. THE IMPACT OF BANNING PHOSPHATI.COI{TAINING DETERÊENTs

0N THE l,lATEB QUALITY 0F rNLA}iD I,¡ISC0NSIN LAKES

Frepared for The Soap and Detergent Association

Nicho'las L. CJesceri, Ph,t.

Bolton Landing, fi.Y, 128i4

February 1983

by

TABLE OF CONTINTS

Executìve Summary

List of Fígures

List of Tables .

I. TNTRODUCTION-..-..

I I. BACKGR0UND-------- _-____-3

A. Lake Phylogeny and Cu'ltural Eutrophication--- -------_-__3B. Nutrient Sources------- ------. __--___-5

C. Liml'ti ng Factor Concept-- ----6D. Nutrient Requirements of Aquatic plants---------- -------lE. Phosphorus Dynamics in Lakes----

F. Bioavailabil ity of Phosphorus-------- ---------LzG. Nature of Detergent Phosphate----- ---18

H. Effects of the control of Detergent phosphorus Inputsto Inland Lakes ----ZA

rII. METH0DS------ __--__---__23

A. Establishment of Field Study Sites---- --------23Lake Selection CrÍteria-------- ----------Zj

. Reference Versus Test Lakes-------- ------ZsDescription of Lakes-

Wastewater Treatment Plar¡ts----- ---------35B. Fjeld 0perations------ ------37

I,later Sampl es------- ---37

Field Measurements and Observations------ ---------39

. C. Chemical Analyses Performed on Water Samples------- ----43

D. Laboratory Bioìog'icaì Analyses------ ----------43Nutrient tnrichment Bioassays ---43

Aìgal Identjficatjon and Enumeration------- -------46E. Statistical Anaiysesl -------47

Covariance Analyses for tach Test Lake----- -------47

TV

Table of Contents (Continued)

Combjned Covariance Analysis for All Test Lakes-----------48

Mul tivarj ate Analysi s/Mul tipìe Comparisons------*---------49

F. Phosphorus Loadings Estìmates----- -----------50

RESULTS-- -,---55

A. Total Phosphorus Concentrations, Chlorophyll a

Concentratjons and Secchi Djsc Depth---- . trtr

Little Bearskjn, Enterprise, Moss, Swan, and Townline-'---55

Teaì, Balsam, Butternut, and Elk------ -----------56

B. Algal Counts and Nutrjent Enrichment B'ioassays --------57

Stat'istical Analysis of Algal Identificatjon and

Enumerat i on Datal -----57

Nutrient Enrjchment Bioassays *----------58

C. Statistical Analyses of Total Phosphorus Concentratìons,

Chlorophyll a Concentrations, and Secchi Djsc Depthsl-----60

Covariance Analys'is for Each Test Lake----- ------60

Combjned Covariance Analysis for All Test lakes-----------62

Mul tivari ate Analysi s/Mul tìp1e Compari sons----- -----------67

D" Phosphorus Load'ings jnto Test Lakes---- ------77

Drscussl0N------ --------,78

A. Phosphorus Loa.ds and the tffects of Detergent Phosphorus on

the Trophic Status of the Test Lakes------'- ----------78

B. [ff ects of Detergent Phosphorus on the Speci f ic l,later Qual i ty

Parameters Total Phosphorus, Chlorophyll a and Secchi Disc

Depth---- ---------83

C. Statjstical Analys'is of Temporal Variations in Green and

1

and Bl ue-Green A'lgal Counts ---'85

D. Phosphorus Residence Times and Lake Response- ---------86

C0NCLUSI0NS---- -----------90\1l.

Table of Contents (Continued)

VI I I. APPENDICES

Appendix A: Maps of Study Lakes

Appendix B: Descript'ion of the [1uìtivariate/MultipleComparison Anaìysis'

Appendix C: Description of the Approach Usäd toDevelop Phosphorus Nutrient Loadings

Appendix D: 1. Precipitation, Runoff Rates, andLand Use Areas for the Test Lakes

2. Phosphorus Nutrient Loads for theTest Lakes

Appendix E: Temporal Variations in Total phosphorusConcentrations, Chlorophyìl q Concentrations,and Secch'i Disc Depths in thã Study l-akes

Appendix F: Secchj Disc Depth and Chlorophyìl a Relation-sh'ips in Townline and Elk Lakes

Appendix G: Temporal Variations jn Green and Blue-Green' Algaì Counts

Appendix H: Vollenweider Loading Criteria

1. The statistical analysis was conducted by John I,l. hlilkinson, Ph. D.,Rensselaer Polytechnic institute, Troy, N.Y.

EXICUTIVE SUMMARY

Summary

of

"The Impact of Bann'ing Phosphate-Conta'in'ing Detergents

on the Haten Quality of Inland Hisconsin Lakes,,

by

N'ichol as L. Cl esceri

February 1983

-qUs$irgThene are 15,000 inland lakes'in the State of l,lisconsin. The impact of

the three-year l,lisconsìn detergent phosphate ban on Hisconsin lake waterqqality has been evaluated through nesearch on l,lisconsin lakes ìikely to beaffected by changes in phosphate d'ischarges. The ban was 'imposed on- Juìyl, 1979 and ended June 30, 1982.

Methodol ogy

"Test" lakes and "reference" lakes were used in the study. The testlakes were chosen as lakes likely to be affected by changes in phospÏãEdischarges to them w'ith'in the three-yean time span of the ban. Therefenence lakes were lakes neceiving negligìb'le amounts of phosphate frornsewage. Data from the reference lakes werõ used to help shäw what changes'in the test lakes wene due to the ban apart from natural effects.

The test I akes were: svran Lake (co'l umb'ia county ) , Moss Lake (vi ì ascounty), Townl'ine Lake (Oneida), Enterprise Lake (Láñglade county), ErkLake (Prìce county, Balsam Lake (l'lashburn county), anã Butternut-Láre(Prìce.County).- The reference lakes were: Litlie Beansk'in Lake (0neidaCounty) and Teal Lake (Sawyer County).

The lakes were studied during the summer of 1978 (befor^e the ban) andduring the summers of 1980, l98l and l9B2 to determind any effects of the ban,

The methodo'logy involved measurìng waten quaììty parametens related toa'lga'l growth: algal concentration (measured by the concentratìon ofchlorophyl1a,ffiment),tota]ph_osphateconcentnatjon(measured by-the concentratjon of aìl pho(estìmated by Secch'i disc depth) and the enumerat'ion and iffi-tlTîcatiõl- ofphytop'lankton. '

Resul tThe total amount of phosphorus entering the test lakes from allsources was est'imated to have been reduced 0.1 to 12 percent as aresult of the ban.

l^fI scON Februany ì983

No changes attributable to the ban in eithen chìorophylì a (algalîonîenlFãîìon) or' total phosphate concentration werä ouservòo inthe test làkes. secchj disc depth readings necorded during thisstudy ane'incons'istent w'ith chlorophyìl a and total phosphãte con-centrat'ions. This 'indicates that other Tactor^s (e.g., suspendedsol i ds , co'l or) were aff ecti ng the Secchi d'i sc depth readi ngs,

The donrìnance in the phytop'lankton of blue-green aìgae (nu'isanceforms) has been on the jncrease s'ince 1978 in both iefeience lakesand test lakes.

Concl usi ons

o There is little liklihood that a phosphate detergent ban couldresult ìn tangible waten quaìity benefits for the vast majority ofI,l'isconsin lakes.

Based on the nesults of this study, diverse soürces of phosphorusand other aìgal nutrients, pìus factons such as'light and tem-penature, are mone ìmpor^tant 'in determi nì ng waten qual ity inHisconsin lakes than the amount of phosphorus controllable by aphosphate detergent ban.

t,.l r 5c0N Februa ry 'l 983

Fiqure Number

I

List of Fiqures

Descrj pti on

Phosphorus Pathways in th.e Environment.

Location of study lakes,

Estimated differences and 95% simultaneousconfidence bounds, effects of post-ban yearsrelated to pre-ban. Data are 1og measure-ments from site L.

Estimated differences and 95% simultaneousconfidence bounds, effects of post-ban yearsrelative to pre-ban. Data are average ôt logmeasurements, sites 1 and 2

tstimated differences and 95% simu'ltaneousconfidence bounds for post-ban year effects.Analysis of test lakes only, log site 1measurement.

Estirnated differences and 95% simultaneousconfidence bounds for post-ban year effects.Analysis of test lakes on1y, ìog geometricmean of site 1 and 2 measurements.

Post-Ban/Pre-Ban differences and 95% confi-dence bounds for difference of test lakes andreference lakes. Site 1 only.

Post-Ban/Pre-Ban differences and 95% confi-dence bounds for difference of test lakes andreference lakes. Log-GM of sites. I and 2.

Balsam Lake (Test) I'lap

Butternul Lake (Test) Map

Elk Lake (Test) Map

Enterprìse Lake (Test) Map

Little Bearskin Lake (Reference) Map

l4oss Lake (Test) Map.

Swan Lake (Test) Map

Teal Lake {Reference) Map

Townl i ne Lake (-les't ) Map

Page Number

10

27

68

69

70

7T

A1

75

76

A1

A2

A3

A4

A2

A4

A5

A6

A7

A3

A8

A5

A6

A7

A8

A9 A9

Figures (Continued)

Figure Number

E1

E1A

E1B

ElC

E1D

E1E

E2A

E2B

E?C

E2D

EzE

E3A

Descri pt'ion

Mean pre-ban and post-ban total phos-phorus concentrations, chlorophyll aconcentrations, and Secchi disc depïhsfor Little Bearskin Lake and its testlakes: Enterprise, Moss, Swan, andTownl i ne Lakes.

Mean p.re-ban and post-ban total phos-phorus concentrati ons , ch'l orophy'l I aconcentrations, and Secchj dìsc depîhsfor Teal Lake and its test 'lakes: Balsam,Butternut, and Elk Lakes

Temporal variation of total phosphorusin Swan and Little Bearskin Lakes.

Temporal variation of total phosphorusin Enterprise, Townlíne, and LittleBearskin Lakes.

Temporal variation of total phosphorusin Moss and Little Bearskin Lakes.

Temporal varjation of total phosphorusin Balsam, Butternut, and Teal Lakes.

Temporal variation of total phosphorusin Elk and Teal Lakes.

Temporal varjation of chlorophyll- ain Swan and Little Bearskin Lakes.-

Temporal variation of chlorophylì aìn Enterprise, Townline, and BearslinLakes.

Temporal vari ati on of chl orophyl'l ai n Moss and Li tt] e B'earski n Lakes,-

Temporal vari ati on of ch'l orophyl l ain Balsam, Butternut, and Teal Lakãs.

Temporal variation of chlorophyll ain Elk and Teal Lakes

Tempora'l variation of Secchi disc depthin Sw-an and Little Bearskin Lakes.

Page Number

E1

E2 E2

E3

t4

E5

E6

E7

E8

E9

E10

El1

812

813

Figures (Continued)

Figure Number

E3B

E3D

t3E

F1

t2

F3

F4

F5

F6

t7

FB

GlA

GlB

G1C

GlD

Descri ptj on

Temporal varjation of Secchi discdepth in Enterprise, Townlìne, andLittle Bearskin Lakes.

Temporal variation of Secchi discdepth in Moss and Little BearskinLakes.

Temporai variation of Secchi discdepth in Balsam, Butternut and TealLakes.

Tempora'l va ri at í on of Secch i d i scdepth in tlk and Teal Lakes

Townline Lake Secchi disc depth (ft)versus chlorophyll a ( ug/L) I978.

Townl i ne Lake Secchi d'isc depth ( ft)versus chìorophyll a ( ug/L) 1980.

Townline Lake Secchi dÍsc depth (ft)versus chìorophyll a ( uglL) 1981.

Townl j ne L.ake Secchi d'isc depth (ft)versus chlorophyll a ( ug/L) 1982.

Elk Lake Secchj disc depth (ft) versuschlorophyll a ( uglL) 1978.

Elk Lake Secchj disc depth (ft) versusch'lorophyll g ( ugll) 1980.

tlk Lake Secchi disc depth (ft) versuschlorophyll a ( ug/L) 1981.

Elk Lake Secchi disc depth (ft) versusch'lorophyll a ( uglL) i982.

Tempora'l variation o'f green a'lgae inSwan and l-i ttl e Bearski n Lakes,

Temporal variation of green algae inEnterprise, Townline and L-ittle Bear-skin Lakes.

Temporal variation of green algae inI'loss and Li ttl e Bearski n Lakes.

Tempor aì varjation of green a'lgae inBalsam, Butternut, and Teal Lakes.

E3C

Page Númber

E14

815

E16

Et7

F1

F2

F3

F4

F5

F6

t7

F8

ul

G2

G3

G4

Figures (Continued)

Fìgure Number

GlE

G2A

G2B

G2e

G2E

Descrí pti on Page Nümber

G5

G6

G7

G8

G9G2D

Temporaì varÍation of green a'lgaein Elk and Teal Lakes.

Temporal variatíon of blue-greenalgae in Swan and Little BearskinLakes.

Temporaì variation of blue-greenalgae in Enterprise, Townliñe, andLì tt'le Bearsk'in Lakes,

Temporal varíation of blue-greenalgae jn Moss and Lìttle BearskinLakes.

Temporal variation of blue-Ereenalgae in Balsam, Butternut, andTeal Lakes.

Temporal variation of blue-greena'lgae in Elk and Teal Lakes.

G10

Tabl e Number

LÍst of Tables

Descrj pti on

Limnologica'l and morpho'logicalcharacteristics of the study lakes.

Muni ci pa1 wastewater treatment p'lant(Wl^lTP) discharges to the study iakes.

Geo'log'icaì characteri sti cs of the testlake drainage basins.

Wastewater treatment plant facilitiesSDA-Wjsconsin Lakes Study.

Years during which inlets, outlets, andwastewater treatrnent p'lants wère samp'led.

Sample handling and preservation procedures.

Physical and chemical ana'lyses performed ateach lake.

Water samp'les col I ected for chem'icalanalysi s.

Procedures for analyses perfornied onwater samples.

Results of nutrient enrichment b'ioassaysconducted i n 1982.

Covariance analysis, Site 1, individualtest lakes.

Page

28

29

30

36

39

6

7

B

6111

t2

13

14

7315

40

41

44

45

5910

Analys'is of variance of the average of the 63logarì'thms of Site I and 2 data.

Proportion of variabi ì'ity expl ained by 63various sources.

Esiimates of the post/pre-ban shift and slope- 66coeffìcient for corresponding reference lakefor the a,reragê of the 'logarithms of site 1 andsite 2 data.

Year average differences of the post-ban yearswith ihe pre-ban year and sinlultaneaus 95percent confidence intervais(C. l. ).Year average diffenences of the post-ban yea.r'swith the pre-ban year and 95 percent simultaneousconfidence intervals(C.1. ) for the differencesbetvreen t.est lake and corresponding referen.eI ake data.

16 74

Tables (Continued)

Table Number

D9

D10

D11

Dt2

D13

D14

015

D16

D17

DlB

019

020

021

022

D?3

024

D25

026

027

D28

E1

Descri ption

Elk Lake Land use areas.

Enterprise Lake precipìtation andrunoff (cm/yr).

Enterprise Lake runoff rates (cu m/s).

Enterprise Lake land use areas.

Moss Lake prec'ip'itatíon and runoff (cm/yr).

Moss Lake runoff rates (cu m/s).

Moss Lake land use areas

Swan Lake precíp'itation and runoff (cm/yr).

Swan Lake runoff rates (cu m/s).

Swan Lake land use areas.

Townline Lake precipitatÌon and runoff( cm/yr)

Townline Lake runoff rates (cu m/s).

Townline Lake land use areas

Balsam Lake phosphorus loads.

Butteinut Lake phosphorus loads.

Elk Lake phosphorus loads.

Enterprise Lake phosphorus loads.

Moss Lake phosphorus loads.

Swan Lake phosphorus loads.

Townline Lake phosphorus loads.

Mean pre-ban and post-ban totalphosphorus concentratj ons , chl orophyl I aconcentrations, and Secchj disc depths -for L'ittle Bearskin Lake and its testlakes: EnterprÍse, Moss, Swan, andTownl i ne Lakes.

Mean pre-ban and post-ban totalphosphorus concentrat j ons , chl oroph.y'l j aconcentrations, and Secchj dìsc depths -for Teal Lake and i ts 'best I ¿kes : Bal sam,Butternut, and tlk Lakes

D7

DB

Page

D6

D7

D9

D9

D9

Dl0

D10

D10

011

011

012

D13

û14

015

D16

017

D18

Di9

E1

E2 t-t:

Tables (Continued)

Tabl e Number Descri ptÌon

Total phosphorus loadings to testI akes due to wastewater and phosphatedetergents.

Comparison of the actual 1978 loadingof phosphorus to the test lakes tocalculated values of Vollenweíder's(1975) permissjble and critical'loadingval ues.

Number of phosphorus and hydraul ícresidence tjmes during the ban and percentof expected change that should be ob-servabl e.

Inlet concentration estimates used inconstruct'ing the nutrient budgets for1978.

National Oceanographic and AtmosphericAdministration weather stations used toestimate precipitat'ion at the study lakes.

Export coefficients (kg P/ha/yr) useclto calculate the 1978 direct drainagephosphorus loadjngs to the test lakes.

Mean yearìy totaì phosphorus concen-t.rations for inlets with considerablemarsh and swamp dra'inage, and wh'ichdo not rece'ive discharges from awastewater treatmenL p1ant.

Balsam Lake precipitation and runoff( cm/yr) .

Balsam Lake runoff rates (cu m/s).

Balsam Lake land use areas.

Butternut [-ake preci p'i tati on andrunoff (cm/yr)'.

Butternut Lake runoff rates (cu m/s).

Butternut Lake land use areas.

tlk Lake precÌpitation ancl runoff(cmlyr).

El k Lake runof f rates (cu rn/:., ) .

Page

7917

18 80

8819

C6

CB

c1

c2

c3

C4

D1

û1

r]2

D3

D3

D4

D5

D1

D2

D3

D4

D5

D6

t7

DB

ci0

cl1

D5

Tables (Continued)

Table Number Descrí pti on Page

cl1G1

G2

Analysis of ca) ln BG; b)

(ee+e ); d) tn

Estimates ofon interceptcomespondi ng'ln Bû, ln G,ln Ip/(1-p)].

ovariance forln G; c) p=86/Ip/[1-p)].pre/post ban effectand slope(s) forreference lake for

p=BG/(ge+e), and

G12

I . I NTRODUCTION

Reductions in the amount of phosphate contained in 'laundry detergents

have been mandated jn some aneas as a means of improv'ing water quality inlakes curnently receiv'ing phosphorus through municìpal wastewater

dischanges or^ septic tank seepage. However, various reports suggest that

such neductions'in deter^gent-related phosphor"us are ineffective in

achi evi ng percept'i bl e water qual i ty 'improvements because the rel ati ve

retluct'ions in the total ìoad of phosphorus to the lakes.ane not signifi-cant, Studies were conducted in l,lisconsin to determine any significant

impnovement in water quality due to a three year ban on phosphate-

conta'i ni ng detengents.

Limitat'ions pr"ohibit'ing phosphor"us in laundry detergents have been

imposed in Nerv York; Indiana; Vermont; Michigan; Minnesota; l./isconsin; Dade

County, Florida; and the City of Chjcago, Illinojs. The State of l.lisconsin

leg'isìated a phosphate detergent ban, effect'ive July 1, lg7g. The ban,

origina'lly enacted to be in effect to June 30,1981, was extended to June

30, 1982. The pu'r'pose of imposing a shont term ban was,to alìow an

assessment of any'irnpact the ban may have had on the water quality of

H'iscons'in lakes rvh'ich rnight lead to a reevaluat'ion of the need for the ban.

The Soap and Detergent Association (SDA)-llisconsin Lakes Study, of which

the 1978 through 1981 sampling programs were a part, yras desìgned to pro-

vi de i nformati on wh'ich woul d contri bute to the 1982 l egi s'lati ve eval uati on

of the !{isconsin phosphate detengent ban. Ìhe study vlould pr.ovide data

which could allow the determination of any s'ign'ificanb changes in water

quality in jnland l,'l'isconsin lakes ìmpacted by munic'ipaì wastewater treat-

l,l I SCON -1- February l983

ment plant dischanges on septic tank/t'ile fie'ld systems. To detenmine the

variab'ility in lake water quaìity that occurs naturalìy, several lakes

which nece'ived neither septic tank system nor municipa"l treatment pìant

dischanges wene included in this pr^ognam. A report evaluating the results

of samples collected dur''ing the 1978-1981 time peniod was pnepared by

N. Clesceri (198i). No posit'ive waten quaìity improvement attr ibutable to

the detergent phosphate ban was observed in any of the study lakes. The

l'lisconsìn Departrnent of Natural Resources (1982) also could not detect any

improvement in inland lake water quaìity. Therefore, t!. purpose of the.

ban was unsupported, From these studies, as well as consumer concern for

effective ìaundry detergent products, the Hisconsin State Legìslature did

not extend the ban beyond June 30, 1982. The SDA-l.lisconsin Lakes Study was

continued in l9B2 to a'llow fon an ana'lys'is of any dernon'strable impi^ovement

in jnland lake water qualìty appearing three years after the ìmposìtion of

the ban.

l¡lI SCON -2- Februar^y 1983

I I. BACKGROUND

0ur knowledge of the compìexìty of freshwaten systems has great'ly

'increased durìng the past 50 years, and efforts ane cont'inuing to advance

furthen our understanding of 'lake pnocesses. Although inland vraters cover

only two.percent of the earth's surface, they pìay an important role in our

society. Increasìng populatjon and demand for improved quality of ìifecontinue to pìace great demands on fneshwater resources. Clean water

suppl ies are requ'ired for drinking waten, recneat'ional act jvjt.ies, and

industrial pnocesses, Appropriate rnanagement techniques can be based on

our undenstanding of the functioning of this precious and vital resounce.

A. LAKE PHYLOGENY AND CULTURAL EUTROPIlICATION

Aquatic ecosystems undergo changes, continualìy evolving as a nesuìt

of their intimate relationship to the surnounciing envinonment, Land use in

the watershed; the age, type, and amount of soi I and vegetati on; rvi I d'l i f e

habi tati on; and popul ati on dens'ity are aì I factons wh'i ch can s'i gn'if i cant'ly

i nf I uence the troph'ic status of a I ake. Lakes generaì ly progr^ess f roln thê

o'ligotrophic state, charactenized by clean, cìear, unproductive water that'is low in nutrients, to a eutrophic state in which nutrients are plentiful,plant and anjmal productivity is high, and water quaìity poor. 0ver ìong

periods of time si1t, mìnera'ls, nutrients, and organic matenials from trib-utaries and other sources accumulate. Nutr ients are necessary for plant

and anirna'l growth, which can eventually lead to a change in the biota of-

the lake. Under natural cond'itions a lake wìl I age sìowìy, decreasing in

l.II SCON -3- February 1983

depth due to the depositjon of sediments, becoming a marsh or bog and

finalìy a terrestrial ecosystem. This process, from start to finish, can

take hundreds to thousands of years. This aging process js called

eutrophìcat'ion, a comp'lex process which varies from lake to lake with

regard to extent, rate, and causal factors. Cultural eutr^ophication is the

accelerated aging of fresh water bodies caused by increased nutrient

1 oad'i ngs due to human act"ivi ti es.

As awareness of the pnob'lems associated with lake eutrophication in

the United States incneased, numenous studies l\,ere undertaken to determine

the causes and characteristics of the probìem (e.g., Chen, 1970;

Mjddlebnooks and Porce'lìa, 1970; Porcella and Bìshop, 1975; and sawyer,

1947). Many remedial measunes are cur-nently being used or investigated.

Some are simply stopgap measures which treat the symptoms rather than the

cause of the water quality degradat'ion. These include coppen sulfate

application to kill aìgae and reduce obnoxious aìga] blooms, alum additions

to prec'ipitate phosphorus from the lake water, and weed harvesting a'imed ab

removing nutrients and the physical hindrance weeds pose to recneatjonal

activities. 0the,n approaches reduce the loadings of nut.r'ients to lakes in

order to cjrcumvent the problems rvh'ich occur once the nutrjents enter the

lake. This has been accompììshed by diventing wastewater flows around

I akes, sewen'ing 'lakeshone aneas which were serviced by indequate septic

tank/tile field systenrs, phosphate detergent bans, phosphorus removal at

wastewater treatment plants, and a number of alter'native wastewater treat-

ment techniques. These latter techniques i¡ìclude using wastewater for

irnigat'ion and as a nutrient source fon croplands and forests, or

discharging it into natural and art'ific'ial weilands which are capable of

l.l I SCON .-4- February ì983

imrnob'ilìzing ìarge quantities

practices can reduce nutrjent

I 975) and urban runoff.

of nutrients. Aìso, improved land management

loadings fr^om both agricultural (l^loolhìser,

B. NUTRIINT SÛURCES

The sources of external (aìlochthonous) nutrient inputs to a lake or

stream can be class'ified as eìther natural or anthropogenic, and point or

non-poi nt.

Point sources include:

Treated yrastes from mun'icipal tneatment pìants and private,

on-site waste disposal systems: domestic wastes, househoìd

food, 'industrial and commercial wastes discharged to mun.ici-

pal treatrnent p'l ants , and water tneatment cherni cal s.

Industrial wastes d'ischarged to waterways.

Stonm sewei" di scharges.

Non-po'i nt sources i ncl ude:

Land runoff.: urban runoff and drajnage, unchannelized storm-

water flows, and runoff from agricultunal lands (e.g., fer-

til jzers, anìma"l wastes, soils, etc.) and forested lands

(e.g., decay'ing vegetation and wild an'imal wastes).

Ground water.

Atmosphere: dryfal 1 ('i . e. , partì cul ates and gases ) and wet-

fal I (i.e. , rai n and snow).

Natural sources of nutr"'i ents resul t f rom geochem'icaì processes and

û

a

o

o

I,I I SC()N -5- February '1983

cinculate v'ia the biogeochem'ical. cycì ing of materials. Nutr"'ients with a

gaseous phase (e.9., carbon and nitrogen) have almost compìete biogeochemi-

cal cycìes, included in wh'ich is a djrect transfer between the atmosphere

and water, whereas nutrients without a prominent gaseous phase (e.g.,

phosphonus, calcium and silica) must be circulated by pnocesses such as

enosion, sedimentat'ion, bioìogica'l activity, and human s0urces, there being

no gaseous atmospheric neservoin on which to draw.

C. LIMiTING FACTOR CONCEPT

The logic of reducing the nutrient influx to natural waters, such that

the nutrient concentration Iimits pìant growth, is based on the functionaì

relationship between pìant productiviby and nutrient avaj'labilìty. The

concept of a l'imjting growth factot" was first intnoduced r'n a concise fonm

by Justus Lieb1g in 1840: "[the.l growth of a pìant is dependent on the

amount of foodstuff whÌch is presented to'it in minjmum quantity" in rela-

tion .to its needs. Th'is tenet has become known as "Liebig's 'Lavv' of the

Mi n'imum".

Although rnany factors such as ìight, temperature, turbulence and

mixing, and nutrients may limit the extent of pìant biomass in aquat'ic

systems, only certain ones, particu'larly nutrients, are contnollable by man

i n a practical and cost-ef fective manner. A I jm'it'ing nutrient can be con-

sidered as such if, when its concentrat'ion in a waterbody is incr'eased, ìtacts to stimulate plant growth and accelerate eutrophication.

Feb rua ry 'l 983|fI sc0N -6-

D. NUTRIINT REQUIRTMENTS OF AQUATIC-PLANTS

Nutrients required for pìant growth are generally separated into two

categories, the macronutrients which are requ'ired in relativeìy ìarge

amounts, and the micronutrients which are needed onìy in minute quantities,

The macronutrients include ca'lcium, car.bon, magnesium, nitrogen,

phosphorus, potass'ium and sulfur. The micronutnients (trace elements)

'include bonon, coppen, 'iron, manganese, moìybdenum and zinc.

Numerous investigations have shown that a w'ide variety of nutnients

can become l'imit'ing to algaì popuìations, but pr.obably bnìy two of the

macnonutrients, nitrogen and phosphor"us, signìficantly control the develop-

ment of aìga'l blooms (Goldman, 1965; Hasler, 19741; and Hutchjnson, lgsT).

The great.est abtention has been focused on phosphonus since it is more

often limit'ing than nìtrogen, and has more read'i'ly control lable sources,

The principal sources of nitrogen for algae are the inorganic forms,

Ì.e., nitrate and ammonia, Fixation of atmospheric nitro.gen by bìue-

green a'lgae and some bacteria, as well as bacterjal degradation of organic

n'itrogen, can al so serve as irnportant ni tnogen sources for aquatì c eco-

systems. Phosphorus 'is generaì 'ly avai I abl e to pl ants onìy as the ortho--?phosphate (P04-") i on, an i norgan'ic form.

Alga'l nequìrements fon both n'itr^ogen and phosphonus are species speci-

fjc. A given concentration of nutrients in one'lake may yield a s'ignifi-

cantìy different algal standing crop than the same concentnatjon in another

lake due to numerous interacting factors, Th. generaì chemicai compositìon

of the water and its alkalinity,'bhe nutrient turnover rate and rate of

degnadation of organ'ic compounds, regenenation from sedi¡nents, and

I{I SCON -7- February ì983

zooplankton and algal excretions, among othen factons, a1ì have some impact

on the aìgal biomass produced in relation to nutrient concentnation. A

good exarnpìe is the'luxury'uptake of phosphonus by natural phytopìankton

popu'lations: "The pattern of phosphorus suppìy and utiIjzation in natural

popuì ati ons of phytopl ankton 'is chanacteni zed by h'i ghly vari abl e rates of

uptake and nelease which bear little apparent r"e'lation to the physioìogical

needs of the pìankton" (Richey, 1977 and lgTg). Taft et al, (1975)

reponted phosphate uptake by Chesapeake Bay phytopìankton rrvas as much as

100 t'imes that required for photosynthesis. Several investigatìons have

suggested that values of 0,01 mg p/L and 0.ì5 mg N/L are the upper con-

centnation limits ìf an ol igotrophic, aesthetical'ly pleasing ìake suitable

for water-based recreat'ion, propagation of cold water fisheries (such as

trout), and vrith very high cìarity is desired; concentnations approximateìy

twice these are the conditions under wh'ich lakes become eutrophic (Chapra

and Reckhow, 1979; D'illon and Rig]er, l97b; and volìenweider, l968).

Typ'icaì]y, aquati c macropltyte and al gaì ti ssues contai n a ratio of

n'itrogen to phosphorus of 15:1, In general, when the lake waten N:p ratiois less than 10:1 nitrogen is limiting, and when it is greater than 14:l

phosphorus js l'irniting.

In conclusion, it can tle stated that tr.lo macronutrients, nitrogen and

phosphorus, generally limit aìga1 growth. However, nutrient tunnover,

organism succession, and water chemistny all interact to make it 'impossibìe

to determ'ine specific Iimìting concentrations common to aiI water bodies,

although general guidel'ines can be established. l,lhen excessìve nutrients

are pnesent'in a ìake, p'lant growth may becorne limited by an extrins'ic fac-

tor such as light.

H I SCON -8- February l9B3

E. PH0!PH0RUS DYNAr'lICS_ IN LAKES

The many dynamic variables that djrectly influence and control aquatic

productivity are intimately related, Not onìy are the material inputs to a

lake a factot', but also the pathways they foìlow; materjals recycìe within

a lake due to comp'lex, interrelated physìca1, biologicaì, and chemjcal pno-

cesses. The major prthways of the phosphorus cycìe are shown in Figure I,All phosphorus originates from minerals which are weathened by nalural pro-

cesses or ut'ilized by humans. Human-nelated activities may increase

phosphorus inputs to surface waters over the natural level expected for a

particular lake. The impact of ány activity on a lake depends upon the

geo'logy, cìimate, morphoìogy, ancl land use characteristics of the basÌn.

The rol e of I ake sedirnents as a si nk 0r sou rce of phosphorus 'is a very

i rnportánt and comp'lex process ì nvol vi ng physi ca1 (e. g, , turbul ence and

mixing), chemìcaì (e.g., redox potentiaì and oxygen content of the

sedinlent-water interface, and the quantity and forrns of iron and alumjnum

'in the sediments), and biologìcai factors (e.g., microbial mineralization

of organi c, phosphorus-contai ni ng compounds ) . Aì though nur¡1er0us rnechani sms

for phosphorus release on uptake from sed'iments are postulated, the manner

'in which they interact, and the resulting net effect, are diffìcultto pnedict or ìnterpret in natunal waters. A few Eeneraì statements are

pertinent concerning the importance of lake sediments in lake phosphorus

dynamics. The reader should refer to other sources (e.g., Hetzeì, lg75)

for a mote complete discussion and list of referenres.

As an illustration of the complex nature of sedinrent phosphon:s,'let

þII SCON -9- Febnuaqv l9il3

OlF\(}ì

rú

pq)

r{tFE5=Ê:oL

(+-

+)cOJÉ:gC)L

I

,ì c)q)l-c+,c

th

fú

=-cpfúo-th=5-ocovto-cÕ-

(l')LCt)

tL

rlirilrI

I

us examine the irrp¡ct of oxygen concentration on phosphorus solubility.Probabìy the r¡ast irnportant point js that there is very ìittle correlationbetween the phosprhirtus concentrat'ion in the sedjments, and the phosphonus

content and prodtrct l v'ity of the ovenly'ing vraters; factors other than simp'le

concentr"at'ion gratli ents and di f f usì on, control phosphor.us exchange between

lake sediments anrl lake waters. Therefore, the phosphorus concentnatìon ofsediments does not provide an indicat'ion of whether. the sed'iments are

actÍng as a source 0r a sink, or whether the phosphorus'is avajlable foraìsar-::;tÏr:;ll'n.r-

poinred out the importancu or u,. con<ritions ar rhe

water-sed'iment intt'¡'f ace and the surface layer of sed'iments (mi cr-ozone) incontrolling phcsPheirus exchange (Mortìmer ì94.l n 1942, and 'lg7l). A rnajor

inechanisrn involvecl in seclirnent-phosphorus exchange is the covalent bonrling

ancl adsorpt'ion of ap,rti te, organi c phosphorus, and orthophosphate to

hydrated iron on aìt¡rninurn oxides (Hjllìams et aì., lgTl)" In the oxj¿ized

state, whiclr occurs ìn the pnesence of oxygen, these compounds are only

sì lghtly solubìe, tvltereas jn the reduced state, r^rhich ûccurs under anðero-

bjc condìiions (absorrce of oxygen), they dissolve more readììy in waten.

0nce phosphortrs is rtlleased the process'is reversib'le, if oxygen.is jnLro-

duced or encountered. The oxygen levels can subsequentìy decrease, con-

verti ng the ox'ides to theì r reduced form, and rel easi ng ihe bountl

phosphorus. This is a cycìe lhat can be encountered over tjme in a lake or

within regions of a lake (i.e., moverirent of cxidized phosphor-us to anaero-

bi c reg'ions on vi ce vensa) .

Therefore, i f n I ake i s oxygerìated the rletal oxi de-phosphonus cornpl ex

'is insoluble and therefore the sediments act as a phosphorus sink. For a

L'{ I STON *11 - Februany 1983

lake wh'ich is ther^mally stratified in summen, if d'issolved oxygen disap-

pears i n the hypo'l i mn'i on, some phosphorus may be rel eased i nto these hyprl-

I imnetic watens. But it is common"ly held that this wateris "trapped" in

this sectìon of the lake during the surrmer because of thermaì'ly-der.'ived

density differences. Because of this, hypolimnetic water, rich inphosphorus, does not come in contact wjth algae'in the epifimnetic zone at

a time when they are present jn the hjghest popuìation numbers and growing

at their fastest rate in the summertime, l,lJhen the lake cools'in the falland the fal I turnover (mix'ing f rom lake bottom to top) occur.s, conditions

(e.g., ìouer temperatures, shorter periods of sunlight) are not conducive

to extensive a'ìga1 growths in sp'ite of potentìalìy higher phosphorus con-

centrat'ions, enhanced by hypo'ljmnetic waters, One ctlntrol1i ng factor inmainta'inìng phosphorus concentrations in lake water relates to the fact

that as turnoven occurs, oxygen, if "it were absent, would be re'introduced

'into the lake water" This oxygen would cause the oxidation of the recluced

metal -pirosphor"us compì ex to the metal oxì de-phosphor.us cornp'lex wh'ich is

i nsol ubl e. Through th'is sequence, phosphorus rel eased f rom sed'iment jnto

over'lying hypolimnebic waters could be returned to the serljments and per-

petua'lìy trappecl.

F. BrrlAyArLABrLrTY 0r PH_OSP[0RUS

All models utjìizing phosphorus con'ceniratjons to estimate algal

growths in lakes assume that phosphonus is the limjting nutrient and that

changes in phosphorus concentrations are reflecLed by changes in algal

growths, Historicalìy, total phosphorus has been used as the index for

T,I I SC(]N -1? - Februa i"y ì 983

such analyticaì models, The proposal of Schaffner and 0gìesby (1978) to

use a cornposjte fraction they term biologicaì'ly available phosphorus (BAP),

whjch represents that port'ion of toial phosphorus uÈilizable by algae, may

improve the accuracy of morlels. By excluding the unusable (unavaiìable)

phosphonus fnactions (e.9,, mìneral apatite) a better relat'ionshjp between

phosphorus and algaì grovrth should result, they argue. A furthe¡- con-

s'idenation was presented in a paper by verhoff and Heffner (1979)

describ'ing a study on the rate of avaiIabiIity of total phosphorus in river

waters: "The majn conclusion to be obtained from this.study 'is the rate. of

convension of total phosphorus to phosphorus available to algae may be more

inrportant than the fraction which would eventualìy becorne avajlable." The

l.rbielis roughly equìvaìent to Schaffner and 0gìesby's BAP, and is often

termed the ultinate BAP. A simiìar opinion was explessed by DePìnto et

al, {1981) in a study on suspended sediments in streams: "An extremely

ìrnporlant factor jn assessment of the biologica'l effects of phosphorus fron

any source is the rate at which the phosphorus becornes avaìlable to aquatÌc

biota within the nece'iving water, This is true, as the rate of convers'ion

of potentialìy-ava'iìable to actually-available phosphorus cornpetes in tirne

with the rale of other processes, for exampìe: adsorption, precipitation,

sedimentation, and dilut'ion," Note that DePinto et al. have 'included the

factors of the tempora'l-spatiaì distr^ibutjons of phosphorus fractions, the'largely unquanti f iable physical-chemical -b'iologica'l transfornlations of

phosphorus species in natural waters, and the cornpìex matter of stream and

'l ake hydroì ogy.

The most "accurate" model would utiIize the actual quantity of

phosphor^us avaìlable to, and utiìized by, algae af any given point in tirne.

t.¡ I SCON -13 - Febrr:ary l9B3

However, frorn the standpoint of appì'ied science, the state of the art of

model ing and the l'im'ited knowledge of the influences refenred to by DePinto

et al., make such a cornpnehensive approach unrealistic at this time. This

is true both with respect to the best ava'ilable technology and ana'lyticaì

techniques for bioìogicaììy availabìe phosphorus, and budgeting con-

s'iderations such as time, personneì, and funds rvh'ich would be required to

undertake such a study. .

Numerous techniques have been deveìoped for the anaìysis of

phosphorus. Each of the methods djscussed below measunes a different por-

tion of total phosphorus; unfortunateìy, no single analysis, or. cornbination

of analyses, adequately represents the phosphorus that is ava'ilable to

algae. Consequentìy, many investigations have been conducted in attempts

to ascertain the best correlation between analyticaììy defined phosphor-us

fractìons and biologica'ììy avaiìabìe phosphorus.

Soluble phosphorus is generalìy cons'idered to be that phosphor^us whìch

can be filtered through a membrane with a 0.45 um pone size; Lhis is often

called "dissolved" phosphonus, although par.t of lhis fraction nray be in

fìne particulates or coll.oids. 'Solubìe phosphorus js usually divided into

two subfr"act'ions, soìuble unneactive phosphorus and soluble reactive

phosphonus. ParticulaÈe phosphorus is that phosphorus which cloes not pass

through a 0.45 rm fjlter.Soluble reactive phosphorus (SRP), often measured by the methocl of

Murphy and Riley (1962), on a mcdificalion theneof, is a fract'ion whjch js

genera'lly considened to be enIirely BAP; a major percentage is usuaìly

orthophosphate (nOO-3). 0rthophosphate is b'ioìogìcalìy the nrost readiiy

t¡sed form of phosphorus, Exper''irnentaì1y, the availabil ity of SRP has been

l-t i 5c0N-14.- February l9B3

shown by DePinto et al. (i980) and Paerl and Downes (1978). Paenl and

Downes separated two fractions from lake vrater by gel fiìtrat'ion; a reac-

t'ive low molecular weight pontion and a neactive high moìecular weight por-

t'ion, the f ormer bei ng irnmed'i ateìy avai I abl e to aì gae whereas the I atter

genera'lly took 48 to 96 hours to be utilized.

Soluble unreactive phosphonus (SUP) is most often calculated from the

djfference between total soluble phosphor"us (TSP) and soluble reactive

phosphorus (SRP) (i.e., SUP = TSP - SRP). At least some of the SUP appears

to be ava'ilable to a'lgae (Berman, 1970; Petens, 1978; a.nd Peters, 1979).

The action of enzymes such as alkaline phosphatases can ljberate phosphorus

f rom ongani cal 1y bound f ract"ions (Berrnan, 1970 and F'i bzgeral d and l'{e1 son,

1966). Us'ing a rad'ioact'ive tracer in phosphor"us kinetics studies, Peters

(1978) suggested 50 to 100 percent of the SUP was BAP in the waters he

studÍed, Furthermore, a complex exchange rnechanism may exist jn the eupho-

tic zone of 'lakes'involv'ing particulate phosphor"us, orthophosphate, an

a.lga1 excreted organic phosphor"us cornpound (XP), and a col Ioiclaì substance

(Lean, 1973a; Lean, 1973b; Petens,1978; and Peters,1979); a port'ion of

the excreted pho5phonus may be in a refraclory forrn unava'iìable to algae

(Peters, 19i9) .

Numerous studies have been conducted to estimate the ava'i1¡bility of

phosphorus in suspended solids of rivers and lakes. Â wide range of BAP

concentnat'ions has resulted, the variab'ility often beìng attributed to the

presence of apatite, a phosphorus rich rnineral which analyzes as tobal

phosphorus but 'is onìy mininralìy utiljzable'by a1gae. Cowen anci Lee (1976)

using åqlenas!_lurn caprjcgllujum in batch bioassayE lasting 19 t't 22 days

found that partjculates fror¡r l4acl'ison, Hisconsin urban runoff releasetl B to

H I SCON -15 - Februa r"y ì 983

55 percenL of the total partìculate phosphorus (Ten) with an average of 30

percent, when suspended 'in phosphorus-free Aìgal Assay procedure (reA,

i971) medium. DeP'into et al. (1981) using their Dual Culture DjffusionApparatus (DeP'into, 1982) analyzed phosphorus avai I abi ì ìty .in suspended

sed'irnents frorn Lov¡er Great Lakes tributaries using se]enaslrunr

-ca.Ll'icorngLgm- and Lake Erie '¡¡ater as a medium jn hanvest-reinoculation

bioassays. The bioassays were cont'inuecl untjl no further phosphorus uptake

was observed, generaì ly three to four werlks. A range of 5 to 31 percent ot

TPP was ut'iììzed, the difference being attributed to apat'ite concentra-

tjons. In stucl'ies using -Ej-ilas!rym_å{Ê.!_q.gr_l_ui!!L jn two-week ìong batch

cultures rvith Provjs'ional Aìgaì Assay Pnocedure synthetic medium (USDI,

1969), Dot'ich et al. (1980) determined that 10 to 31 percent (¡¡ean = 21

pencent) of TPP rvas BAP jn sed'itnerlts frorn the drajnaqe water of Bìack Creek

w.rtr:rshed, Al len County, Indiana.

'0ther rvork has been undertaken to relate BAP to chemicalìy anaìyzed

phosphorus f ract'ions. The r:ornponents rif Total s.edirnent phosphor"us rvith

sign'i lican'L' nelal jonsh'ips to BAP are rnainly associaled wjth lhe reactive

l'{a0H-extracLable fraction (NaOH-P on base extractab'le, react.ive) (Depìnto

eL a'|., 1981; ',.lilìiams et al", 1gB0; anrl coyren ancl Lee, 1976), A citrate-di't'hionìte-b carbonate exlractable (coa-e or reductant extractable) frac-tion has also been relaIed Lo tsAP, howeven, neither js a rjirect measui-ernen.f

of tsAP. Portions of these fractions, 13 to 77 percent of NagH-p and 14 to

24 percent of CDB,P, have been found to be BAp.

Data on the bjoava'ilability of phosphorus (tcr aìgae ancl aqualic

macnophytes) in wastewater tre¿tinent p'lant ef f I uenbs i s scarce, De pinto

et al . (l982) conducted a1 gaì bi oassays us'ing vrastevrater samp'les f rorn

H i SCON *l 6- February 1983

several locations (untreated influent, intermediate effluents, and "final"effluent) in foun treatment plants. These pìants were located in areas

where phosphate detergent bans were in effect (the Gates-Chiì'i-09den Plant

in Rochester, N.Y,; the Frank Van Lare Plant in Rochester, N.y.; the Big

Sister Creek Plant in Angola, N.Y.; and the Eìy Plant in Ely, Mn.). The

results of the Dual culture Diffusìon Apparatus (uepinto et a'|., lgSz)

bioassays suggested an average of 72 percent of the total phosphorus in the

bioassay samples was BAP. A comparison of the samples from different

locations in the treatment trains indicated that the proportion of totat

phosphorus which was BAP usual]y did not vary significantìy as wastewater

passed through a plant,

An indirect means to investigate the bioavailability of phosphorus in

wastewater treatment pìant effluents is to look at the degnadation of

various forms of phosphorus which ane not readily used by algae. The

extent to which treatment processes convert these phosphorus compounds to

orthophosphate (which is available to algae) can be considened an indirect

meôsure of bioavailability. One class of compounds generaìly considered to

be unutilizable untiì hydrolyzed is condensed phosphates (Sutton and

Larson, 1964 and Clesceri and Lee, 1965 a,b). The rate of hydrotytic

degradation of condensed phosphates is influenced by many factors,

including temperature, pH, enzymes, co]loidat gels (e.g., hydrated oxides

of iron and aluminum), comp'lexing cations (e.g., ca'lcium), concentration,

the 'ionic environment of the soìution, and bioìogical activity. Studies on

the kinetics of the hydroìysis of pyrophosphate and tripo'lyphosphate

(condensed poìyphosphates) in steriìe and non-sterile lake water and algal

culture media showed that the chem'ical hydrolysis of these compounds was a

l¡l I SCON -17 - February l9B3

reì ati vely sl ow process, whì I e b'i ochemi cal hydroìys'i s proceeded rapi dly

(Clescer i and Lee, '1965a). 0then stud'ies also have neported that the pre-

sence of organisms in solutions to which condensed phosphates were added

caused an accelerated rate of hydrolysis of these phosphates (Karì-Kroupa

et a'|.,.l957; Sawyer, .l952;

and Engelbrecht and Mongan, l95g). A phosphate

balance performed on the Oxford, England activated sludge wastewater treat-ment p]ant (Lewin, ]973 and Perry et aì.,1975) showed that mone than 90

pencent of the condensed phosphates wene hydrolyzed to onthophosphate in

the sewers. 0nly ì.5 percent remained in the settled sewage, and none was

detectable in the final effluent. This plant was not equipped fon chemical

phosphorus removal.

Much is yet to be'learned about the bioavailability of phosphorus in

dìffenent waters. Further work rnust be undentaken to clanify r¿hìch what

forms of phosphorus are being measured by the vanious anaìyt'ical tech-

niques, which of these forms are immedìately available to algae and othen

onganisms and the tÍme (and under what conditions) it takes others to

degnade to a usable form, and how these various forms of phosphonus affect

the even-changing physical, chemical, and biotic environments of lakes and

streams.

G. NATURE OF DETERGINT PHOSPHATE

A typicaì alì-put'pose househnld detergent is made up of +.he surfac-

tant, the phosphafe buiìder, and mjscellaneous ingredients, such as bright-

enens, perfumes, and inhibitors. The surfactant portion \{as responsible

for past foaming probìems caused by the non-biodegradable ABS

r{ I sc0r{ -18- February l9B3

(branched chain a'lkyì benzene sulf,onate). The ABS surfactant was replaced

mone than a decade ago with biodegradable LAS (straight chain, or linear

alkyì benzene sulfonate).

Tripolyphosphate is the chemical of choice as a phosphate builder in

the all-punpose household detergent. Phosphate effectiveìy ptays many

diverse roles as a detergent builden. One function is to soften water by

sequestering caìciurn and magnesium ions which would othenwise react with

fatty soils to form insolubìe curds, thereby preventìng the surfactant por-

tion of detergents to emulsify the fatty soils. Phosphates also sequester

objectionable elements such as iron and manganese salts that can cause rust

spots, Jelìowing, or other dìscoloration of laundered fabrics, i.e., iron

and manganese are changed to an.'insoluble form which deposits on cìothing.

tlith phosphate, the iron and manganese remain in solution and are rinsed

away. Phosphates also disperse and suspend dirt. l,lithout phosphates, dirtpartic'les get trapped in fabric; w'ith phosphates, di rt particles with nega-

tively charged phosphate ions attached. repel each other and stay suspended

in the wash water. Detergent phosphate builders also emulsify grease and

promote micelle formation. Additiona'lly, they provide alkalinity which is

necessary for effective soil removal; perspìration, food residue, and other

acid soils interfere with optimum detergency. Phosphates in detergents

provide buffering capacity t,hat maintains an ideal range of alkalinity

whìch provides good cleaning action. Too high or too low alkalinity can

cause damage to textile fibers, dyes, eqiripment, or skin. Good cleaning

requi res the mai ntenance of al ka'li ne condi ti ons. Tri po'lyphosphate has the

attri bute of simul taneously carryi ng out a'l 'l these essenti al functi ons. At

the same time, it fulfills the other requirements of a bu'ilder inaterial in

HI SCON -l 9- Febru¿ ry i 983

detengents in that it is (i) non-toxic, (ii) mild to skin, (iii) harmless

to equipment, (iv) safe for textiìes, (v) easiìy removable in wastewater

treatment, (vi) compatible wìth other detergent ingredients, and (vii) eco-

nomical to consumers.

H. EFFECTS OF THE CONTROL OF DETERGENT PHOSPHORUS INPUTS TO INLAND LAKES

The reasoning behind the control of phosphonus'inputs to lakes is

that any reduction should ultimate'ly affect water quality, if the system

is ìimited by phosphorus,

Schaffnen and 0g'lesby studied l2 New York lakes to compare different

methods of calculat'ing phosphorus loadings and to develop reìat'ionstrips

among phosphorus and chlorophyll a concentrations, and Secchi d'isc depths.

(Schaffnen and 0glesby, l97B and 0gìesby and Schaffner, .l978) Ch'lorophyll a

data on six of the lakes from their study, covering pre- and post-ban

periods for phosphate detergents in I'lew York State, wene used by Trautman

et al. (1982) as an example of the use of their statistical methodology for

determin'ing data requirements fon assessing lake restoration programs, In

an ana'lysis of each lake jnd'ividua'lìy, the authons concluded that two years

of pre-ban data were insuffic'ient to demonstrate a change in post-ban

ch'lorophyl I a 'levels, "no matter how many years of post-ban data could be

obtai rìed. " T.lhen Trautmann et al . emp'loyed thei r stat'isti ca'l ana'lysi s to

the lakes as a group they concluded there was a pnobability of only 0.7

percent that a chlorophyll A drop at least as large as the one observed

would have occurned by chance; they attributed this drop to the phosphat.e

detergent ban. Cause and effect was not established, howeven. The data

HI SCON -20- February '1983

showed essentially no correlation (R2 = 0.001) between the per.centage drop

'in chlorophyll a and the authors' estimates of the percentage drop in the

avajlabìe phosphorus load for the six lakes studied.

Anot,her study was conducted'in Indiana by Bel'l and Spacie (1978). îo

study the effect of a 1973 detergent-phosphorus ban'in Indiana, 15 lakes

wene chosen fnom the Environmental Protection Agency's (EPA) National

Eutrophication Sunvey (NES) list. Data collected in 1977 wer-e compared to

1973' but no sign'ificant difference in water qua'lity changes could be

observed between lakes that received wastewater and those that did not.

The reason given was that the phosphor^us contribution from detergents was

small compared to other phosphorus sources. A similar conclusion was

reached in a study of six l4innesòta lakes (Runke, lgBZ).

Stud'ies by Etzel et al. (1975a, b, c) also observed that the Indiana

ban yielded little reduction in stream phosphor^us. They concluded that the

"remaiiring strearn phosphonus levels [during the post-ban period] in r-egions

rece'iving significant treated-sewage discharges ôre still far too high [forthe ban] to be of any b'iological consequence".

Prior to implementation of the Hisconsin phosphate <letergent ban, the

tPA (1978) projected the impact of the ban on'inland lakes of the state

using data gathered in the NES. Twenty-one Hiscons'in lakes included in the

NES were seìected that received wastewater thal, was not treated for

phosphorus removal and for which nutnient joadings could be determined.

All twenty-one lakes selected were eutrophic. To predÍct the impact of the

phosphate laundry detergent ban on the lakes, a 50 percent re<luction in the

mun'icipal wastewater treatment plant phosphorus load was assumed to result

from a phosphate laundry detergent ban (approximateìy two times the pnesent

r{ I st0N -21 - Februa ry '1983

day average). Mathematical models were then used to predict the impact of

such a phosphorus neduction on the water quality of the twenty-one lakes.

The report projected that 18 of the 21 ìakes evaluated would show no obser-

vable changes in waten quality and would, thenefore, remain eutrophic. Italso stated that observable changes in water quality wouìd be expected at

two of the lakes (Lakes Delavan and l,lapogasset). The effect of the ban on

one Iake (Buttennut) could not be predicted since the primary productivity

in the ìake appeared to be limited by light or some factor other than

phosphorus or nitrbgen (Butternut Lake was one of the lakes Ín the

SDA-Wisconsin Lakes Study).

t-lI sc0N -22- February 1983

I I I. METHODS

A. ESTABLISHHENT OF FITLD STUDY STTES

Lake Selection Criteria

Lakes receiving direct or indìrect discharges of effluent from

wastewater treatment p'lants on septic tank system seepage, and reference

lakes receiving no point sounce wastewater dischanges nor having high num-

bers of septic tank/tiìe field systems located on them, wene studied.

Descriptions of the lakes initiaì'ly chosen for the study, some of which

have subsequently been eliminated from the program, can be found in the

protocoì for the 1978 study (SDA,1978), The selection of lakes was based

on the best state-wide data available at the time the lakes were chosen.

In the first year of study (1978), water quality data were collected

on twelve llisconsin lakes. During the course of that sampling year, infor-mation'was received whÌch indicated that furthen sampìing should be discon-

tinued on two of the lakes because.of the enactment of programs which would

affect water quaìity and interfere with the interpretation of study

results. These two were Shawano Lake in Shawano County, where the take's

shone was sewered, and l{oquebay Lake in Maninette County, where an exten-

sive weed hanvesting program was conducted during 1.978,

Due to water quality trends, and drainage basin and lake charac-

teristics dissìm'ilar from Swan Lake (e.9., aquatic weed dominance in Fish

Lake versus phytoplankton dominance in Swan Lake), sampìing of Fish Lake, a

reference ìake, was not continued after 1981. After analysis of the lake

data, Little Beanskin Lake was substituted as a suitable reference lake

IJISCON -23- February 1983

f,or Swan Lake.

Although Delevan and Hapogasset Lakes were oniginal'ly identified by

the EPA as lakes most l'ikely to change because of the ban (EPA, undated),

they were excluded from this study because of impending plans to impìement

phosphorus removal at the municipal treatment systems at both sites during

the study period. Several other candidate lakes wene el'iminated fon the

same reason.

Only 'lakes thought to have the potential to be impacted by phosphorus

'loadings from nearby municipal treatment pìants or septic tank systems were

chosen. Lakes receiving at ìeast 30 percent of their annual phosphorus

'load from nearby municipaì treatment pìants, as reported by the NES, were

considered for inclusion in the study; for lakes not'included in the NES,

discussions with ï,lisconsin Department of Natural Resources pensonneì

(Research Bureau and Inland Lakes Renewal Program) were held to ascertain

the suitabiìity of candidate point source and septic tank system lakes.

0ther lake selection criteria included the folìowing:

0n1y natural lakes were selected; impoundments were excluded from

c on s i de nat-i on.

Because the phosphate detengent ban in Wisconsin was originally

f or two years, lakes rvith retention times no greater than two

years were selected. The minimum acceptable retention time

was 30 days.

In selecting 1akes, consideration was given primariìy to those

lakes for which prev'iously collected data were available from

such studies as:

1.

2.

3.

HI SCOr{ -24- February 1983

â. The Natjonal Eutrophication Survey (NES)

b. I^|'isconsi n DNR Quanter'ly l4oni tori ng Program

Select'ion was restricted to those lakes with depths of three

meters or more.

Lakes were selected wh'ich had the pubìic access required for a

ì ake sampl i ng program.

Preference lvas g'iven to lakes which had at ìeast one, but less

than four sìgnificant tributaries. This criterion allowed for a

reasonable monitoring program of the tributaries to be conducted.

Proponents of the l.Iisconsin phosphate detergent ban contended that the

water qua'lity of lakes jn the noçthern part of the state would be protected

by the reduced phosphonus input'resulting from the ban on phosphate

detergents. Lakes in the nonthern part of the state were neported to have

good water qua'lity and, theoretically, would be pnotected fnom eutrophica-

tion and water quaìity degradat'ion by a ban on phosphate detengents. In

considerat'ion of th'is, most of the lakes chosen for study were in the

northern region of the state.

Reference VersrJs TestJakes

Observable water quaì'ity cf,ungus due to naturaì causes (e.g., cìimatic

variations) are known to occur from year to year. Thenefore, a means to

distinguish between effects from natural causes and those of the phosphate

detergent ban had to be established, Th"e approach used by this study was

to compare the water quaìity of test lakes, which rece'ived municipal

wastewater effluent or septic -cank seepage, to reference lakes which

received a minimal phosphonus load'ing from these sounces. By comparing

4.

5.

6.

H I SCON -25- February .l983

water quality changes in these two types of lakes, shifts in the water

quality of a lake receiving municìpal or septic tank/tile fieìd phosphorus

loadings could be distinguished from natural changes. The project design

was based on the assumption that natural changes (mostìy cìimatic) affect

both types of lakes in a similar manner. To enhance similanities in

natunal effects, reference lakes were chosen that were located in the same

regìons of the state as test lakes and had monphoìogical and watershed

characteristics similar to the test lakes,

Description of Lakes

Figure 2 shows the locations of the lakes selected for this study.

Figures Aì through A9 (Appendix A) are maps of each lake. Tables ì,2 and 3 summarize the pert'inent limnologica'l , morphoìogìca'l , and geological

characteristics of the lakes, and wastewater treatment p'lants discharging

into the lakes or their tributaries. The test lakes were Swan, tlk, Moss,

Townl'ine, Butternut, Baìsam, and Enterprise; the reference lakes were

Little Bearskin and Teaì.

1, Sv¡an Lake is located in Columbia County i.n the south centrál

region of llisconsin. The Fox River enters the lake at the

eastenn end and ex'its at the westenn end. The area surrounding

Swan Lake is partially developed, although major portions are

marshy and unsu'itable for development. Shoreline development in

1981 consisted of 88 residences, foun townhouses containing four

unjts each, and a goìf course, The major land use in the

dra'inage basin is agniculture. The Pardeevi I le Municipal

Hastewater Treatment Pìant discharges 'into Spring Lake, about

b.l I SCON -?6- February .l983

Test Lake

Reference Lake

aA

Location of Study

-27 -

Aeal

gugernut tP'

e@Bal sam El k

@

Li ttl eBearski n

_€Lnterprl se

ÐSwan

Figure 2: I akes

ïaþle 1: Llmnologlea I and morphologica I characteristícs

La ke

Su rfaceArea (a)

(ha)Volume (b)

( 10l++6 cu m)

Mea nDepth ( c )

(m)

of the study

Max i mumDep th

(m)

I a kes.

Mea nHydraul icRes ídence

ïime (days) (d)

Tríbutaries Fe)

ln OutShorel ine

Leng t h( km)

Ba I sam

Butte rnut

Erk

Enterprise

Moss

Swa n

Tovn I fne

Little Bearskin

Tea I

107

400

36

194

76

163

61

63

405

8.74

't7. 10

o.5,

7.26

2.36

16. 03

2.'t5

1.57

16.15

8.2

4.3

1.5

3.7

3. 'l

9.8

3.5

.2.5

4.0

67

184

2

600

860

178

270

300

15

10

6

9

9

25

6

B

9

2

4

1

1

0

1

?

'l

2

1

1

1

1

1

'l

1

1

1

't1.9

18. 0

9.8

5.3

10. 5

3.4

6.8

16 .9

(a): surface aneas were based on values from planimetry of u.S.G.s. topographic maps, data avai lable fromthe wisconsin DNR, and data presented on clarkson-cornpany'mãpå fiauxauna, Wisconsin).(b): Volumes \r'ere estimated using bathymetric data provided on clarkson Compâny maps.(c): The mean depth equats the lake votume dívided by the surfâce area.(d): Th¡s \r'as ca lcu.l ated usíng estímated f lovs for an average year (mean annua l) precipitation ancl runoff(see nutríent budget methods), and lake volume estimatés "based'on bathymetric data and surface âreas.(e): lntermittent streams are not I ísted as tributaries.

-28-

Tabre 2: Municipar wastewater treatment prant (V.lV.lrp)discharges to the study lakes.

LakeMunicipal

County WWTP

Type ofDisposal for

Treated Sewage

Barsam washburn Birchwood Land DisposalButternut Price Butternut Ind.irect Discharge

to Surface Water

Etk Price Phillips Direct Dischargeto Lake

Enterprise Langlade None Septic Tank/TiIe Fields

Moss Vilas Lac duFlambeau Land DisposaL

sv¡an ,

columbia Pardeeville tti.å;::.:å=;:î:i"

Tov¡nline oneida Three Lakes rndirect Dischargeto Wetlands

LittIeBearskin Oneicla None None

Teal Sawyer None. None

-29-

Table 3: Geological characterísrics of the test lake drainage basins (a).

Base (ßF) or Low (LF) So¡ I permeabí I iry

Ba I samLa ke

ËtkLa ke

Tovn I i neLa ke

Buùternut BUtternut andLake Sp i l ler Creek:

Sandy loam.

si lt loam. Mud andSclìnur Lake lnlets,and Easterrì shore:fine, sandy loam.

Di rect Dra inage:f i ne, sandy I oam.lnlet Dra ¡nage:No rthe rn Reg ¡ on -f i ne sandy I oam.Soutlìe rn Reg ion -s¡lt loam.

D I rect Dra i nage:sandy l oam.Town I ¡ ne Cr. : pea t,some fine sandyI oam and f i ne sand,Maple Lake: finesandy I cam.

End morainc (tlll, sand,arr<l gravel) and pittedouLwa sh ( sand an<i g rave l );100 to 150 feer thick.

Al I glacial dríft 150 to2O() I'eer. thick. Aroundlakc: ouLvash ând ¡ce-contâct deposíts (sand, sandand gravel ). Perimeter ofbasin: end moråine (t¡tl).P¡tted outvash (sand andgravel ); âbout 100 feetthick.

Sa nd s tone,undifferentiated.

lgneous andmetamorph ic.

I gneous andmetamonph ic,und i ffe rent i a ted .

I gneous andmetamorphic.

Ground moraine (ctay, si lt, tgneous and LF: O.qO - 0.59sand, gravel, anrl boulders) metamorphic,about 100 feet, thick. undifferentíated

Pítted outwash (sand and lgneous andgravel ); 100 feet thick. metamorphic,

und i ffe rent ¡ a ted.

LF: 0.16 - A.29

LF: about 0.40

BF: <1.0

o.8 - 2.5

0.2 - 0.8

o.B - 2.5

West lnlet:o.a5 - o.ztRest:o,B - 2,'

Enterprise Fine sandy loam.La ke

MossLa ke

F i ne sand.

Swan Lake Sandy loam andI oa nty sa nd, somes¡lt loam.

Direct Drainage; glacial Sandstone. LF: <0.3lake deposíts, 0 to 100focb ttìick. Fox Rivcr inletDra inage: ground morâ ine,100 to 200 f'eer t,h ick.

Lr: û.40-0.59 5-10

o.2 - 2,5

no data 2,5-'Strat,if ied drift, outvashand ice-contact depos i ts( sand, sand ând g rave I )about 100 feet thick.

( a ) Sources:

(b) Enterprí{11 tllisconsin ceologicat and Natural Hist,ory Survey(2) Ulited States Deparrment of Agricutrure (197S).

se ând Tovnl ine Lake values vere meãsured under a O.5

(1916 a,b;.1927;'1947; and 1959).

inch head (oakes and cotter, 1968).

-40-

three miles upstream on the Fox River,

Swan Lake was 'included in the National Eutrophication Survey

(NES, 1974b) and was part of the l,lisconsin DNR monitorjng program

during 1975, 1976 and 1977. Additional water quaìity data ane

available through the Inland Lake Renewal program.

2. Elk Lake is located in price county in the north central

region of l.liscoRsin. At the southeastern corner of the lake is

the lone inlet (from Lake Duroy), and at the northwestern end is

the outlet (to Long Lake). The city of phill'ips adjoins the take

along its entire southern shone. In 1981, there lvere seven

residences, three'industries, and a beach aìong the shore'line.

tf f I uent from the Phi I l'ips Mun'ici pal Wastewaten Treatment Pl ant

js djschanged directly to Elk Lake.

The H1scons i n DNR col I ected lvater qual 'ity data f rom El k Lake

twice during L977. Elk Lake was included'in the NtS, but a final

report was not prepared.

3. Moss Lake is located in vilas county in the north central

region of l'lisconsin...The lake has no ìn'let, and one out'let, a

culvert unden the road separating I'loss Lake from Long Interlaken

Lake. The shoreline is part'ial]y deve'loped with 40 residences

evident in 1981. The land surroundìng the lake is ìargeìy

forested, although some swampy areas are present; agr.icultura'l

activities are insignificant. Lac du Flarnbeau uses a stabiliza-

tion pond, located approximately 0.4 km from Moss Lake, for

l,lI SCON -3't-- February I 983

4.

wasteþJater tneatment. Present'ly, the pond is operating as a

seepage cel l.The l,l'isconsin DNR collected waten quaìity data on Moss Lake

in 1975,1976 and 1977. The lake was not included in the NES.

Townìine Lake is located in 0neida County in the north

central region of llisconsjn. The lake has two inlets, Townline

Creek and the South Inlet; the former dnains a large swamp into

which the Three Lakes W}.ITP effluent is discharged, and the latter

receives the fìow from Maple Lake. There is an outìet to

Plant'ing Gnound Lake along the northern shore. In I981, there

were 7ì residences along the shoreline, The land immediately

surrounding Tovrnìine Lake is ìargely forested.

Townl'ine Lake receives effluent indirectìy, vja an inter-

ven'ing marsh, from the Three Lakes l,lastewater Treatment Plant.

The Three Lakes plant is new but does not have phosphorus removal

capabi I ities.

No water quaìity data are current'ly available from the

H'isconsi n Dt{R, but the lake was 'incl uded i n t}re l{tS (Uf S, .l974c),

5. Butternut Lake js located in Price County in the north

central regì on of l,l'iscons jn. The lake has four inlets and one

outlet. The Schnun's Lake inlet 'drains Schnun Lake which is

neanìy 100 percent developed; the Mud Lake jnlet receives its

water ìargely from several swampsi the Spilìer Creek inlet is fed

by runoff from forested and agricultural lands in 'its lower

reaches, and swamps in the upper reg'ion; and Butternut Creek

l.l I SCON -32- February l9B3

6.

receives runoff from forested, agricu'lturaì, and swampy lands.

The Butternut Þlunjcipa'l Wastewater Treatment Plant discharges its

effluent into Butternut Creek less than two mi'les upstream of the

I ake.

In 1981, the shoneline is over' 50 percent developed with

eight resorts and 185 residences, There are a few farms with

pastures in close proxirnity to the lake, as well as several

swampy regions.

An EPA report (fRR, undated) indicated that Butternut Lake

might show observable water quality changes as a result of the

phosphate detergent ban. The t,lisconsin DNR collected water

quality data on Butternut Lake during 1973, 1974 and 1975. The

I ake was stud'i ed unden the (NtS, 1974a) .

Balsam Lake is located in Washburn County in the north-

western region of Hisconsin. The ìake has two inlets, one from

Birch Lake at the northeastern end, and one fnom Mud Lake aìong

the central portion of the eastern shorel'ine. The outlet to Red

Cedan Lake is at the sóuthern end of the lake. The shol^eline is

only sparseìy deveìoped with about 24 residences located on steep

banks aìong the lake. The lake is surrounded by heav'iìy wooded

hills (birch, aspen, mapìe and a few conifers). The City of

Birchwood Municìpaì ldastewater. Treatment Plant seepage ceìì

system is located in the Balsam Lake drainage bas'in; there is no

direct di scharge to any sunface wat,ers.

The Hisconsin DNR col lected water quaìity data on Balsam

H I SCON -33, February .l983

Lake duning 1975,1976 and 1977. The lake was not included in

the NES.

7. Enterprise Lake is located in Langìade County in the

northeastern regìon of ifisconsin. The lake has one tributary on

the western end drain'i;',,.: â Sizabìe marsh and swamp, and an inter-. mittent tributary drain'ing another large swamp located near the

southenn shore of the lake. The outlet is on the northern side

of the lake.

Approximateìy 50 percent of the shoneline is developed with

a Boy Scout camp and 104 nesidences. In addition to the two

large mansh and swamp aneas already described, the surrounding

land contains numerouS swamps and manshes situated among the

forested h'ills; agricultural land is vi rtual ìy non-existent.

Enterprise Lake was chosen to represent northern lakes

rece'iv'ing phosphonus through septic tank seepage and receives no

mun i ci pa'l wastewater ef f I uent.

The lake is part of the Inland Lake Renewal Program and was

samp'led by the !,li sconsi n DNR during 1973, 1974 and 1975. It was

n ot i ncl uded i n the llES.

8. Little Bearskin Lake is located in 0neida County in the north

centnal region of t.I'iscons'in. Bearskin Creek enters the lake on

the nontheastern side and ex'it's at the eastern end. In 1981,

there were 43 resi dences a'long the shorel i ne. The smal I dna'inage

basjn is ìargeìy forested w'ith some aneas of marsh and swamp,

Little Bearskin Lake was used as a reference lake for Swan,

I,tI SC0N -34- February ì983

tntenprise, Townline and Moss lakes.

The tlisconsin DNR colIected wat,en qualìty data on Littìe

Bearskin Lake during '1973, 1974 and .l975.

The lake was not

included in the NES.

9. Teal Lake is located in Sawyer County 'in the northwestenn

'region of Wisconsin. The inlet from Lost Sand Lake is on the

westenn end and the out'let, the Teal River, is on the

southeastern side; a tributary, Lynch Creek, enters on the

northern shore. In 1981, thene wene residences and four nesort

build'ings aìong the shorel'ine but the lake receives n0 discharges

fnom wastewater treatment pìants. Teal Lake was used as a

reference lake for Baisam, Butternut and Elk lakes,

The tl'isconsin DNR colìected water quality data on Teal Lake

during ì975, 1976 and 1977. The lake was not part of the NES.

Wastewater Treatment Plants

Brief descriptions of the wastewater tneatment pìants discharging

d'irectly on indjrectìy to the test lakes are pnesented in Table 4. The

process descriptions are accurate for the period fr^om 1978 through 1982.

-35-l,l I SCON February '1983

TABLE 4: l,lastewaten Treatment Pl ant Faci ì itiesSDA-lJisconsin Lakes Study

Pardeevil ler.ï'isconsin (Swan Lake)p rl tna ny setf I I ngh'igh-rate tnìckl ing fiìterseconda ry settì i ngchl oni nati on(no process changes 1978-82)

Thlee Lakes, t¡liscons'in (Townl ine Lake)Wrotati ng bi o'logi cal contactorseconda ry settl 'i nganaerob'ic sl udge di gesti ons ì udge dry'i ng bedschl ori nati on(no process changes 1978-82)

Lac du Flambeau, l,ljsconsìn (Moss Lake)

(onigi nal 'lagoon was 11 acres in 1978,and was expanded to three ce'lìs total-i ng 17 ac nes 'i n 1979 )

Phil I jps, l^l'i:cons jn (Elk Lake)ffiloy¿-rate trickl ing filtersecondary settl i ngchl ori nat i onanaerobjc sludge cligestion(no process changes 197S-82)

(Butternut Lake)

(no process changes 1978-82; is nowaerated lagoon w'ith seepage pits)

Bi nchwood, l,li sconsi n (Bal sam Lake)ffi'secondary settl ingseepage pits(no process changes 197S-82)

Butternut, l,li sconsi n

pnìmary settl ingstabil'ization pondchl o¡'i nat'ion

-36-

B. FIELD OPTRATIONS

Hatgr llampl es

Two or three sampìing sitesn one of which was the deepest site on a

ìake, were chosen for each lake. Lake sampling commenced as soon as

feasible after ice out (within a week aften spring tunnover) and terminated

at falI turnover. Eight sampfing trips r,rere made during this time period;

twice per month in July and August when aìgaì growths are generaìly the

most rapid, and appnoximateìy once pen month for the rest of the peniod.

During alì years an integrated, two-meter sample of the surface water was

obtained at each sjte by rneans of a .|.5 inch diameter PVC pipe. The sample

was taken by drawing a rubber stopper into the'lowen end of the pipe with a

ì ength of nyl on rope, securing the stopper' ìn position. l,lhere the ther-

moclìne ('ident'ified by means of a temperature probe read every meter) was

less than two meters, the ìntegrated sample was taken on'ly above the ther-

mocline. In addition to these sampìes, a volume proportional sample r,las

collected at the deepest s'ite during 1978, l9B0 and l98l. Based upon the

calculation of waten volume, and the percentage of the total water volume

each lake stratum repnesented, water samp'les were collected at l0-foot

intervals with a 2-liter Kemmeren water sampler, and composited to form a

volume proportional sample. To ìnsure that suspended sed'iments near the

lake bottom did not contaminate the sample,. the sampler rr{as ìowened no

closer than one meter above the sediments.

Grab samples of discharges from the Pardeeville (Swan Lake), Three

Lakes (Townline Lake), Ph'ilìips (Elf late) and Butternut (Butternut Lake)

wastewater treatment pìants were colìected during each samp'ling trip.

I{I SCON -37 - February l9B3

Information on effluent flows was collected from records of the }{isconsin

DNR and/or from the treatment pìant operators. Since the phosphate

loadings frorn septic tank systems around a lake are scattered and generally

diffuse, individual septic tank systems were not sampled in this study.

Lake tributary and outìet samples were collected durìng many sampìing

trips. The s'ite locations and the years sarnpìed are presented in Table 5.

Additional sampìes were obtained duning the weeks of July 19, August 2

and August 19, ì982, for furthen nutrient analyses and for use in the algal

nutrient enrichmerit bioassays. These consisted of additional port'ions of

the ìntegrated surface sample at the deepest site of each lake.

All sampìe bottles were vlashed with phosphorus-free detergent, rinsed

with distilled water, and indelibly labeled with an ident'ification card

which conta'ined the location of the sampìe and the date, Bottles wene used

for th'is project on'ly and were labeled with a project'identification code.

trdater samples were preserved and stoned from the time of collection until

anaìyzed (Table 6).

Fi el d l-'leasurements and 0bservati ons

The date and tjme sampìes r{ere collected at the deep site, the general

weathen conditions, the air temperature and any unusua'l conditions were

reconded on field sheets duning each sampling tnip. Depth pnofiles of con-

ductivity, water temperature and djssolved oxygen were taken at the deepest

site on each lake at one meter intervaìs; Secchi dìsc depths were measured

at al I I ake s'ites (faUl e 7) .

Although Secchi disc measurements have been a tr^aditional parameter in

limnoiogical field studies for many years, its usefulness as a sunrogate

H I SCON-38.

February '1983

Table 5:

Lake

Years during which inlets, outlets, and wastewatertreatment plants were sampled.

Years Sampled

Swan LakeFox River InletFox River Outlet,Pardeeville WWTp

EIk LakeIn1et from Lake DuroyOutlet to Long LakePhillips WWTP

Townline LalieTownline CreekSouthern InletNorthern OutIetThree Lakes WWTP

Balsam LakeBirch Creek InletOutlet to Red Cedar LakeInlet from Mud Lake

Butternut LakeButternut Creek InletButternut Creek OutletSpiIIer Creek InletButternut WWTPMud Lake In1etSchnur Lake Inlet

Enterpri se LalceWestern InletNorthern Outlet

Moss LakeOutlet to Lonqr Lake

TeaI LakeLynch Creek In1etTeaI River InletTeal River Outlet

Litt1e Bearskin LakeNorthwest InletBearskin Creek InletBearskin Creek Outlet

1978,

1978,

1980,

1980,

1981, !gB21981, ]-gB21981, I9B2

1981, LgBz19811981, ]-9B2

1981, L9g21981, !9921981, IgB21981, !982

1981, t9B21981, 7gB21981

1981, !9821981, tggz1981, lgg21981, t9B219811981

1981, IgB2L9B1, I9B2

1981, lgg2

1981, !9821981, !982L9B1, IgB2

l_981 , 79821981, lgB21981, l9B2

7978,

1978,

T978,

i978,

1980,

1980,

1980,

1980,

t978,

T978,

1980,

1980,

-gg-

Table 6: Sample handling and preservation proced.ures.

Handling andParameter Bottle Type Preservation

Total Phosphorus Nalgene Stored at(amber, 60 mI) 4 deg. C on j-ce.

Nitrate+Nitrite-N Nalgene Stored at(amber, 500 ml) 4 deg. C on ice.

Ammonia-N

Total Kjeldahl-N

Alkalinity

Total Filterable Nalgene Filtered in thePhosphorus (amber, 500 ml) field (O.45¡m

membrane filter),Filtered Ammonia-N stored at 4 deg.

C on ice.Filtered TotalKj eIdahI-N

Filtered Nitrate+Nitrite-N

pH Nalqene Stored at4 deg. C on j-ce.

Chlorophyll a None Filtered in thefieId, (O.45;lmmembrane filter),filter stored atless than 0 deg. Con dry ice.

AIgaI Identification Glass Lugolrs solotion(amber, 100 ml) added in the field.

-40-

TabLe 7: Physical and. chemical analysesperformed at each lake.

Deepest OtherParameter Site Site{s}Secchi Disc Depth + +

Surface'Temperature + .

Surface. Dissolved +Oxygen

Dissolved Oxygen +Profi Ie

Ternperature +Profi le

ConductivityFrofiLe

-41 -

measune of a'lga1 growth, chìorophyl I a and tr"ophic status remains a contro-

versìal subject (Car'lson, 1980; Edmondson, l9B0; Lorenzen, ì980; and

Megard, l9B0). The Secchi disc is designed to measure the transparency of

water; Secchi disc depth decreases as alga'l growths increase. Howeven,

numerous othen factors also affect the Secch'i disc reading:

e The Secch'i disc loses accunacy as aìgal growths become low.

o There is considerable variability among different observers.

o Light is attenuated by particulates other than aìgae,

e The s'ize of the particles suspended in the vrater column varies;thereby affecting light attenuation.

e The natural coloration of iake water due to the presence ofdissolved substances varies (e.9., brown lakes whose color origi-nates from naturalìy-occurring humic substances).

e Su rf ace 'l i ght i ntens i ty.

In evaluating the results of Secch'i disc readings it should be kept

in mind that the chlorophyll a should have an ìnver^sely proportional rela-

tionship wìth Secchi disc depth. If this is not the case, then any

observed increase (or decrease) in Secchi disc depth is most ìikeìy due to

a decrease (on increase) in light attenuation due to one of the other fac-

tors mentioned above.

Secchi disc depths ane usually recorded to the nearest foot or half-

meten, thereby intnoducing mone vagary into the measurement. A complete

discussion of the use of Secchi discs can be found in Hutch'inson (1957).

l¡lI SC0l{ -42- February 1983

C. CHEMICAL ANALYSES

The ana'lyses performed on the surface water sampìe collected at the

deep site by means of the lwo-rneter integnated water sampìen uras ana'lyzed

for the parameters listed in Table 8; the integrated sarnples collected at

other sites on the lakes were analyzed for the same parameters, except for

alkalinity and total Kieldahl nitrogen. The volume pnopontional samples

were analyzed for only total phosphorus. All the analytical techniques are

presented in Table 9.

A pontion of the integrated surface samples collected from the deep

sites of the lakes during the fourtlr, fifth, and s'ixth sampling tnips Ìn'.l982,

was filtered in the field through a 0.45 !m merxbrane filter and ana-

I yzed fon the f o'l I owì ng:

a Total filterable phosphorusc' Fi I [ened ammoni a ni trogení' Filtered total Kjeldahl nitrogen (TKN)c Fi I tered n'itrate/ni tri te ni trogen

These data were used in the nutrient enrichrnent bioassay stud'ies.

D. LABORATORY BIOLOGICAL ANALYSES

Nutri eLt En rj_cllment llgg!¡ays

Nutrient enrichr'¡ent bìoassays r^rere conducted to ascertain which

nutrient(s) llmited the growth of algae'in the study lakes during the peak

productivity period of Ju'ly and August, 1982. For these studies, an addi-

t'ional portìon of the two-meter integrated samp'le was collected on the

scheduled sampìing trips during the weeks of "luly 19, August 2, and August

l^J I SCOH -43- February 1983

Table B:

Pa ramete r

Water samples col lected for chemíca I ana lys¡s.lake samples vere tvo-meter íntegrated samples,treatment plant samples were grab samples.

Unless othervise specllied aland tributary and \dastevater

1978 tô 1O81 1 982

Deepest Othe rLa ke La keSite Site(s) Tríb. WWTP

Deepest Othe rLake LakeS¡te Slte(s) Trib. Wl-tTP

Tota I Phosphorus

Totâ I Phosphorus(volume prop. )

O rthophospha te

Nitrate+N¡tnite-NAmmon i a -N

Tota I Kjeldahl-N

Total FilteredPhospho rus

F i I tered Ammon la

Filtered TKN

Fi ltered Nitrate+Nirrire-NAlkalinítychlorophyl I a

pH

+

+

+(a)

Not App I icab I e

++Not Appl iceble

+-+-

+

+

+

+

+

+

+

+

+

+

+

+

+

+

+

+(â)

+-+-

+(a)

+(b)

+(b)

+(b)

+

+

+

+(c )

+(c)

+(c)

+(c)

*¿

+

+'

+

+

.t

+

+

+

(a ):(b):(c):

Not in 1978.Not in 1978 or 1980.Peak product ¡vi ty samples. only on the 4th, 5th and 6th sampl ¡ng tr¡ps, 1982.

-44-

Table 9: Procedures for ana lyses performed on vater samples,

Tota I Phosphorus

Orthophosphate Phosphorus

Nitríte + Nítrate Nitrogen

Ammonia Nitrogen

Total Kjeldahl Nitrogen

Alkaliníty

pH

Dissolved Oxygen

Chlorophyl I a

Phytop lankton ldent í f icat íonand Enumerat,ion

Transpa rency

Standa rd Methods ( 1978 )EPA Methods (1979-'t982ì

Strickland & Parsons: Murphy & Ri leyTechnique (1978)EPA Methods ( 197!-1982)

Strickland & Pãrsons: Cadmíum-Reduction Method (1978)EPA l,lethods | 1979-1982)

Standa rd Mcthods: I ndopheno I

Me thod ('t979 |EPA Methods (1979-19821

EPA Methods ( 1978-1982)

APHA et at. (19751u.s. EPA ( 1979)

Strickland & Parsons (1968)

u.s. EPA (1979)

Str¡ckland & Parsons (1968)

u.s. EPA (1979)

APHA et at. (1975)

u.s. EPA (1979)

U.S. EPA 11976 and 1979)

APHA et at. 11915)

/\PllA er a l. 11975J

Stanclard Methods: Títrimetric APHA et al. (19751Method s

Standard l,lethods: Glass Electrode

Standard Methods: Winkler Methodv/i th Azide Mod if icationStandard Methods: Trichromatic Methods APHA et al. (1975)

Standard Methods: Sedgevíck Ral"ter Cell API1A et al. (1975)

Secchi disc

-45-

.l6. Triplicate cultures of Selenastrum capricornutum were established for

each of the follow'ing additions for each lake:

l. Controls: no additions, lake water on'ly.

?. Enriched with 50 ug P/L using KHZP04.

3. Enriched with 300 ug N/L using ammonium nitrate.

4. Enniched with 50 rg P/L and 300 ug N/1.

5. Enriched wìth 2 ¡g/L Si02, using NarS'i0, x HrO.

6. Enriched with 1 mL tnace metal solution, no EDTA.

7. Enriched with 1 mL tnace metal soìution, EDTA added.

8. Enriched with 50 þg P/1, 300 rg N/1, 2 ng/L Si02, 1 mL trace

metal solution, and EDTA.

A Turner l,lodel I I I fl uorometer vlas used to neasure fl uorescence. A gi ven

nutrient, or set of nutrients, was consjdered to be enriching if it pro-

duced at least 25 percent greater fluonescence than the controls during the

fi rst àeven to ten days of the study" The three sets of experiments were

conducted for ìì, 12, and 20 days, respective'ly.

Al gal _ Identif ica:L'ion -and Englerqtion

One sample per ìake, taken at the deepest samp'ling site, was col'lected

during each sarnpìing trip for jdentification and enumenatjon of the algal

species. Samples wene obta'ined from the lake surface by means of the two

meter integrabed waten sampler and wene preserved in Lugol's solutjon"

I-II SCON -46- February .l983

E. STATISTICAL ANALYSTSl

Three forms of statistical analysis r,rene penformed; (j) covariance

analysis for each test lake separately, (ii) combined covariance analyses

for alì test lakes, and ('iii) mul'[ivariate ana'lysis obtaìning mu'ltiple conr-

parison estjmates for pre- and post-ban differences of interest.

Comparisons wene made between the test and reference lakes using the

ìogarithms of the measunements of total phosphonus (TP), Secchi disc depth

(SD), and chlor"ophyl'l g (Chl .g). For each of these forms, an analysìs was

done for the data from Site 1 (the deepest portion of the lake) and the

avenage of logarithms of Sites 1 and 2.

Covariance Ana_lysis for Each Test Lake

For each test ìake, a covaniance anaìysìs rvas penformed us'ing the

model:

log yti = [o * Ê1 log y.. + cZ Bi + Ei

whe re:

yti represents the 'i-th observation on the test lake

yri represents the corresponding i-th obs.envatìon on thereference lake

Bi is a durnmy varjable with value 0 for pre-ban obser-' vations and value I fon post-ban observations

In this analysis,the quantity of interest i.s,r, which repnesents the post-

ban shift in the test lake response after the modelled relationship with

the reference lake has been considered.

lThe stat j st'ical analyses were conducted by John ld. l,li I k'i nson, Ph.D, ,Rensselaen Poìytechn'ic Inst'itute, Troy, N.Y.

}II SCON-47 - February ì983

Combined Covariance Anal.vsis for All Test Lakes

For a simultaneous examination of all test lakes, a covariance analy-

sis was performed using the model:

los vri = 3o + Ê1 loe Jri - r!,

oj Dji - r!,

,j Dji log yri

6+ S Bi + f . D.. B. + F

¡=f 'i -ii "i -i

where:

and

] as follows:

q%D3&q5%Swan100000Balsam 0 1 0 0 0 0

Butternut001000Elk 0 0 0 1 0 0

Enterprise 0 0 0 0 1 0

Moss0'00001Townline 0 0 0 0 0 0

In the above model, looking at groups of terms from left to right, the

f- O for pre-ban observationsBi =

f-]. fo. post-ban observations

i- O for pre-ban observationsDii =f

l' for post-ban observations

r^¡ ISCON -48- Februany ì983

interpr^etation is as follows. The log test ìake nesponse can be considered

as the sum of a generaì'intercept, â linear component relatìonsh'ip with the'log refenence lake response, an adjustment in the intercept for the speci-

fic test ìake, an adjustrnent in the s'lope for the specific test ìake, an

adjustment in the generaì intercept for the pre/post-ban, and an adjustment

in the'intercept fon a specific test lake for the pre/post-ban. An analy-

sis pantitioning the test lake response variability into assignable sources

ì n the order I i sted was penformed,

Mu]ti variats Alaly:i s/Mul ti pl e Comp_ani sons-2

A generaì mul'[ivariate analysis taking into account the covariance

structure of the data v¡as carnied out. It compìements the preceding two

anaìyses by using statistical procedures which account for poss'ible corre-

lation of the measurements.

To this end, the measurements fon total phosphonus for a given lake

and year were considered to be a single multìvariate variable, or vector,

for purposes of analysis. For each post-ban year, the vector analyzed

actualìy cons'isted of the d'ifferences from the cornespond'ing sampling times

for the singìe pre-ban year. In one ana'lysìs, the test lakes and the

reference lakes þlene considered 'together, In another ana'lysìs, the test

l akes r{ere consìdered sepanate'ly. In eithen case, the vectons of d'ifferen-

ces Ìtere analyzed'in a two-way tabìe in which the entrjes wene identified

by lake and by year. Sìmultaneous confidence intervals on the djfferences

were also constructed. Several analyses were done for the logarithms (to

Zþle r.¡ould like toT.A. Delehanty wÍth

r^l I SCON

acknowledge the assistance of A.S. Paulson andthis mult'ivariate anaìys'is.

-49- February l9B3

base 10) of Site 1 measurements, and for the average of the'logged Site 1

and Site 2 measurements. The analys'is was repeated for chlorophyll a and

Secch'i dìsc depth. A deta'iled descnìption of these analyses is given in

Appendix B.

A similar anaìysis was also perfonrned for each test lake us'ing the

d'ifferences of the logarit.hms of the test lake measurernents and the

corresponding reference lake measurements -- in a sense, an anaìysis of the

test lake data adjusted for potentia'l re'lationship with its conresponding

reference lake.

In additìon to the above, simu'ltaneous confidence intervals were

constnucted for differences of the yearly averages between the post-ban

years and the pre-ban year.

F. PHOSPH(IRUS LOADING ESTIMATES

Phosphotus loadings to a lake can be segmented'into tributary input,

direct drainage and atmospheric input. The tributary input would result

from any runoff f,rom areas which eventua'lly terminate into a stneam

dra'ining into a lake. I,iastewater-der"ived jnput would account for both

sevrered areas which have discharge poìnts into the lake direct'ly, or a tri-butary to the ìake, as welì as septic tank/tile fie'ld system seepage or

systern fai I ure. Di rect drai nage woul d ari se fnom areas di rectly adjoi ni ng

the lake shoreline, aneas which do not drain to a lake tribuLary, but

rather drain to the lake itielf. Fon atrnospheric load'ings, onìy the wet-

fall and dryfalì which enter the lake surface area direct'ly are included.

Thus, the total of these inputs would compnise an estimate of the combjned

l,lI SCON -50- February l983

phosphorus loads to a lake from various sources. A contplete description

of the calculations involved in estjmating phosphorus loads

during this study are presented in Appendìx C; the gener"a'l procedures are

described below. ll,l'ith these phosphonus loadings available for the deci-

sìons regarding waber qua'lity questions can be more adequate'ly addressed,

Phosphorus loadings to a lake can be segmented into tributary input,

dì rect drainage and atrnospheric 'input. The tributary "input would result

from any runoff from aneas which eventualìy termjnate into a stream

draining into a lake. Wastewater-derived ìnput wouìd account for both

sewered areas which have djschar"ge points into the lake directìy, or a tri-butary to the ìake, as well as septic tank/leach system seepage on system

fajlure. Direct drainage would arise lnom areas dìrectly adio'in'ing the

lake shoneline, areas whjch do not drain to a lake tributany, but rather

drain to the lake'itself. tor atinospheric'loadìngs, on'ly the rvetfall and

dryfall which enten the lake surface area directìy are included'in this

category. Thus, the total of these inputs would comprise an estimate of

the conlbined phosphor"us loads to a lake from various sources. A cornpìete

description of the calculations jnvolved in estimat'ing phosphorus loads

during this study are presented in Appendix C.

The ar^eas drajned by streams and lakes, and land use aneas, wene deli-

neated by surface morphoìogy as provided in the most recently updated

U.S.G.S. topograph'ic maps.

Stneam flows were determined utiliz.ing data presented'in the hydro-

ìog'ic budget sections of the U.S.G,S.-Univers'ity of ll{isconsjn Geologicaì

and Natural History Survey hydroìogic atìases (0ìcott,1968; Young and

Hi nda'11 , 19721, and 0akes and Cotter, 1975) , supp'lemented by norma'li zed

l,II SCON-sl -

February I 983

stream flows calculated by the U.S.G.S for the National Eutrophìcat'ion

Survey (NES) and Nat'ional 0cean'ic and Atmospheric Admj n'istration (N0AA)

monthiy precipitation neports for t.l'iscons"in.

The procedure for determìning runoff quantit'ies ancl flows involved

cal culating a runoff to pr"ecip'itatìon ratio for each year. The value of

thjs ratio for an average yean's pr"ec'ip'itation vvas obtained from the

U,S,G.S.-Universjty of l,.ljsconsin Geologicaì and Natura'l History Survey

hydro'logic atlases or from strearnflows pr^ovided by the U.S.G.S. to the NtS,

To conrect fon the diffenence between the precipitation of a test yean and

that of an average year', an assumption was made that the pr^oportion of

runoff to precipitat'ion could be mocleled by the average basin data for dry,

average, and wet years.

Lake trjbutany phosphorus Ioad'ings rlrere estimated usìng fIows and the

rnean yearìy phosphorus concentnations of the tr"ibutaries. For streams

..recei v'i ng muni ci pa'l waster¡rater treatment pl ant ef f I uents, the I oadi ngs

attributed to the streams were determjned by subtract'ing the treatment

plant load'ing frorn the tobal measuned stream load.

Loadings to treatment pìants r,rere assumed to be 1.36 kg P/yr(3.0

lbs P/cap/yr) for untreated wastewaten contaìning detergent phosphorus and

0.96 kg p/cap/yr(2.1 lbs P/cap/yr) for untreated wastewater wjthout detergent

phosphorus (SDA, unpub'lished data). Phosphorus removals due to treatment

þ/ere considered to be 10, 20, and 90 percent fot'pt''irnary, secondary, and

chemical phosphorus rernoval treatments, respectìve'ly, and 100 percent for

seepage cells and lagoons.

No direct field measurements were made

loadings, thenefore several assumpt'ions were

of septic tank/tile field

rnade. The resul ts of the l9B2

-52-

shoreline survey (SDA) were used to estimate the number of septic tank/t'iìe

fieìd systems jn use. The survey results are presented in the lake

descniption section. All lakeshore dwellÍngs (hornes and cab'ins), resorts,

and camps were assumed t,o have septic tanks (undoubtedly an overestima-

t'ion). Resonts and camps were consídered to be the equ'ivalent of 10 and 20

dwellings, respectively, and to have seasonal occupancy on1y. 0ther

dwel'lings were est'imated to be 50 percent seasonal and 50 percent year-

round residences. A year'-round occupancy of 2.5 persons was assumed for

each dvlel'l'ing or dwel I'ing equì val ent; seasonal occupancy was cons'idered to

be four months pen year. The per" capìta phosphonus load to septic tanks

was assumed to be the same as fon mun'icipal treatment plants. (The value of

1.36 kg P /cap/yris probabìy hi gh for seasonal res'idences whi ch may not

have laundry facilitjes or other modern applìances). A phosphorus removal

of 90 percent before the discharge entered a lake was used for non-fa'iìing

septi c tanks, wheneas fai I ì ng sept'ic systerns r,.lere consi dened to have no

phosphorus removal capability. A septic tank failure rate of 10 percent

''{as used.

For atrnosphe.rì c phosphorus I oadì ngs (both wetf al I a.nd dryfaì ì ) , the

value of 0.175 kg P/\a/yr reported in the NtS studies was used s'ince'it

appeared to be a conservative value. More recent studies (Reckhovr et al.,1980) conc'lude that the NES value probabìy underestimated the actual

loadings, l,leather statjons lvere chosen on.the basis of precipitatìon data

prov'ided in the U.S.G.S. - Universjty of Hisconsin Geologica'l and Natural

Hìstory Surveys (0lcott, l968; Young and Hindall, 1972; and Oakes and

Cotten, .l975), and the average (year) pnecìpitatìon data in N0AA climatolo-

gi caì reports.

hJI SCON -53- February ì983

Direct dnainage (the area surrounding a ìake which contributes runoff

di rectly to the lake rather" than a tributany) 'loadìngs r,lene calculated

using export coefficients compiìed by Reckhor¡¡ et al. (1980) and the nespec-

tive coeff icients were app'lied to spec'if ic land use areas. The choice of

coefficients was based on precipitat'ion and nunoff quant'ities, the areal

extent of ind1vidual land use types, soìl and geologicaì data from the

U.S.G.S.-Universìty of Hjscons'in Geologicaì and Natural H'istory Sunvey

atlases (0lcott, 1968; Young and l-l'indall , 1972; and Oakes and Cotter,

1975) , soiì survey neport,s (l,l'iscons'in Geo'logical and Natunal H'istory

Survey, 1916 a,b, 1927,1947 and 1959; and U.S.D.A., 1978), types of vege-

tation, and field observatiolts. The export coefficients rrlene genera'lìy

chosen from the lovrer end of the concentration range presented in the

litenature whenever data from mone than one study were ava'ilable, thereby

yielding conservatively low estinates for direct runoff.

l,l I SCON -54- February '1983

IV. Resul ts

A. TOTAL PHOSPHORUS CONCINTRATIONS, CHLOROPHYLL A CONCENTRATIONS, AND SECCHI

Tables E1 and E2 summarjze the total phosphorus and chlorophyll a

concentrations of samples collected in the fjeld and Secchi disc depth measurements

made in the fjeld. Table El contains the average values for these parameters from

Little Bearskin Lake, a reference lake, and'its respective test lakes: Enterprise,

Moss, Swan and Townljne Lakes. Table E2 contains the same ìnformation on Teal Lake,

a reference lake, ancl its respecti've test lakes: Balsam, Butternut, and tlk Lakes.

Figures 1-3, A-E in Appendix E are graphica'l presentations of the rnonth'ly mean

values of the three parameters. The follorving js an overview o't the changes jn

these parameters.

Ljltle Bea-rskin, Enterplise, l"loss, Sw{n, a.nd Townline

In Little Bearskjn Lake annual mean total phosphorus concentrations were

consistently higher (average of 40 percent higher) in the ban period (1980-82) than;

before the ban (1978). Chlorophyll a levels were in genera'l, slightly higher during

the ban period. Secchj disc depths were an average of about 20 percent greater.

In the ban perìod total phosphorus concentratjons r^¡ere much greater (more than

doub'led) ìn Enterprise Lake than in the pre-ban period. Moss, Swan, and Townline

exhibited higher phosphorus concentrations'in the first full ban year, 1980, but by

1982 all three exhibited reduced phosphorus.concentrations compared to the pre-ban

samp'ling year. This trend jn these latter three jakes did not appear to occur in

Ljttle Bearsk'in Lake, the reference lake.

-55 -

Chlorophyll a concentrati0ns averaqed about 50 percent h'igher in tnterprise Lake

during the ban period compared to the pre-ban period. Chlorophyll a concentrations

remained relatìvely unchanged in Moss Lake throughout the study. Chlorophy'I1 a

concentratjons viere higher in the Swan Lake during the first two ban years,1980 and

i981, but were s'l'ightly lower in 1982 compared to the pre-ban perìod. In Townline

Lake, a very sf ight 'increase in chlorophy'll a was observed in the first tv¡o ban

years, but a declìne relative to the pre-ban period was observed in 1982, the th'ird

year of the ban.

Secchi dìsc depth measurements averaged about 20 percent greater in LittleBearskin Lake in the ban period compared to the pre-ban perìod. Simjlar'ly,

Enterprise, l,loss, and Townline Lakes also exhibited greater Secchi disc depth

readìngs in all three ban years,1980-82. Swan Lake, after exhibjting an increase

'in Secchi d'isc ctepth in the f"irst full ban year, 1980, showed reduced read'ings the

succeeding two ban years

Tea1,, Balsam, Butternut, qnd Elk Lakes

Teal Lake, a reference lake, exhibited hìgher 'lotal phosphorus concentrations

in all three of the ban years compared to the pre-ban period. Chlorophy'll {concentrations were relatìve'ly the same in 1978 and 1980 in Teal Lake, but were

h'igher in 1981 and i982. Secchi disc depth readjngs were'about 50 percent higherin

1980 compared to 1978, but declined to about 1978 levels by 1982.

Simjlar to Teal Lake, bolh Balsam and.Butternut exhjb'ited hjgher total

phosphorus concentrations in the ban period compared to the pre-ban period. tlk

Lake exhjbited higher total phosphorus concen'[rations in 1980, but the concentra-

tions in i9B1 and 1982 were lower than pre-ban levels.

-56-

Both Balsam and Butternut exhìbited higher chlorophyll a concentrations jn

1981, but lo\{er concentrations in 1980 and 1982 comparecl to pre-ban concentrations.

Elk Lake exhibited chlorophyll a concentrat'ions more than double the 1978 levels in

al I three ban years

All three test lakes (Balsam, Butternut, and Elk) exhibited greater Secchi disc

depth measurements in all three ban years compared to the pre-ban perìod.

The data obtajned on the three parameters during the field study were

stat'ist'ical ly ana'lyzed to cletermine if any improvements or deterjorat jons beyond

those observed in the reference lakes occurred ín the test lakes. The results of

that analys'is are presented'in Section C

B. ALGAI" COUNTS AND NUTRIENT TNRICHI'ITNT BIOASSAYS

StatjsLical _Analysis ol-j-lçlal Identificatjon and Inumerat'ign Data

F'igures GIA through G1E (Appendix G) show the temporal varíatjon in green algae

over the course of the study. The monthìy means of the counts of green algae are

plot.ted. Figures G2A through G2E are sinlilar pìots for bìue-green a1gae. It'isreacliìy apparent from these figures that both qreen and blue-green a'lgae steadììy

increased in numbers in both test and reference lakes throughout the study.

Ana'lyses were conducted on 'logarithms of blue-greens (ln BG), logarithms of

greens (ln G), p = BGIBG+G) and ln [p/(l-p)]. The transformations, where used, r{ere

for obta'ining better agreement with the distributjonal assumptions for the varjous

analyses. The use of log'istic transformat'ion, 'ln [p/(]-p)], v¡as of marg'ina1 value.

Tables Gl an<J G2 (Appenclix G) represent covariance analyses like those done for

total phosphorus, chlorophyll a-, and Secchi d'isc depth, 0bserve in Table Gl, for

all measurements consjdered, that Lhe apparent tracking of the test lakes by the

reference lakes js accountìng for a substantial amount of the total variabil'ity.

Even so, except for the greens, the post-ban effect is statjstjcalìy significant

-57 '

(a'lthouch not dramatícalìy so). In Table G2, you will observe that this post-ban

effect'is primarily assocíated rvith Elk Lake, wjth Butternut also appearing for the

blue-greens. In both'instances, the dìrection is associated with increases in the

blue-greens that þJere greater than corresponding reference lakes

Nutrient Enrichment Bioassays

A summary of the results of the 1982 nutrient enrichment bioassays conducted

us'ing samples from all test lakes is presented in Table 10. When'interpreting the

bioassay resu'lts, it should be kept in mind that if the P and P+N treatrnents (but

not N) induced a'lgal growth, then phosphorus was most l'ike1y the causative agent;

s'imilar'ly, whenever both the N and P+N treatments (but not P) showed aìgai growth

stimulatjon, then the addit'ion of nìtrogen was most'lìke1y the causative factor.

In mid-Juìy, stirnulation was observed in only Balsam Lake and Elk Lake water

samples. Both lakes supported'increased a'lga'l biomass v¡hen enriched wjth silicate

alone,.or an addjtjon of phosphorus and nitrogen. Additionalìy, phosphorus alone

stjnrulated aìga1 qrowth in Balsarn Lake during the mid-July period.

In early August, phosphorus enrichment alone yie'lded ìarger standing crops in

waters from Balsam, Butternut, Elk, and Enterprise Lakes; nìtrogen additjons alone

increased gro,rrth in Townlìne Lake; simultaneous addit'ion of phosphorus and nitrogen

stimulated biomass levels in Balsam, Butternut, tnterprise, Moss, Swan and Townljne

Lake waters. In additìon, trace metals appeared to be stimulatory in Butternut Lake

wa te r.

The results of the mid-August tests vrere very sìmìlar to the ear'ìy August

experinents. Hower¡er, silicate alone stimulated growth in tlk Lake water and

nitrogen alone'in Townline Lake l^iater, and trace metals no longer were observed to

y'ieìd greater algaì b'iomass in Butternut Lake. tlk Lake water was stimuìated by

phosphorus as wel I as a phosphorus and nitr^ogen add jtion. Lastly, Tor¡¡nl jne Lake

-58-

Table 10:

0PN

P&N

SiTM

Lake

Results of nutrÍent enrichment bioassaysconducted in 1982.

Key (a)

No effect observed by any treatment.Stimulation with phosphorus enrichment.Stimulation with nitrogen enrichment.Sti-mulation with the simultaneous aciditionof phosphorus and nitrogien.Stimulation with silicate enrichment.Stimulation with trace metalenrichment.

Week of Samplins, 1982

July 19 August 2 August 16

Bal sam

Butternut

Etk

Teal

P, P&N, Si

0

P&N, Si

0

P,P&N

P, P&N, TM

P

P, P & N

&N, Si

6(N

P,P&N

P,P&N

P,P

P,P

Enterpri se

Moss

Swan

Townline

LÍttle Bearskin

o

0

o

o

P&N

P, P & N P, P & N

&N

&N

P&

&N

P&N

P&N

P&N

N, P&N

N,

P,

P

P

P, N,

P,N,P

N

,si

(a), A combination of P andsuggests phosphorus orre spective Iy.

P&N, orNandP&N,nitrogren stimulation,

-59-

a'lso responded to a phosphorus addition (as well as a nitrogen and phosphorus and

ni trogen add'i t'ion ) .

A comparìson of the nutríent enrichment studies, algal counts, and chloro-

phy'l1 a analyses provides valuable'insights'into alga1 community dynam'ics in these

lakes. llle are espec'ia'lìy interested jn Swan Lake since more than 10 percent of Íts

1978 phosphorus load could be attributed to detergent phosphates.

In Swan Lake, a bloom consisting of two diatoms (Cyclotella and llsgj-larje) and

a cryptophyte (Cryptomona.s) occurred in earjy May, 1982, fo'llowed by a lesser growth

of blue-greens (Anabaen{ and Aphanizomq¡pn) and a green alga (Ankistrodesmus) in

June. Durìng the months of Juìy, August and September, the lake's waters were

dominated by bìue-green algae, y¡ith peaks jn late July of Anabaena and Chrooc_occus,

and in mid-September of Apheli¿lrìgryI- and Chroococcus; betleen these blooms, a

significant decline in cell numbers was observed (m'id-August). The nutrient

enrichment bioassays, aìgai counts, and chlorophyll a analyses agreed well. The

numbers of algal cells and chlorophyll a concentrations stabilized'in late Juìy and

remajned fairly constant throughout August. Thìs was the period when bioassays

i nd j cated that an addi tion of both nì trogen and phosphorus rìras necessary for a'lga'l

growth to be stjmulated. It would be approprjate tr: conclude that both nitrogen and

phosphorus are ìniportant nutrjents for thjs lake

c. !uI_srl_cA!_ J_ryausrs oI rornt pHospHo

CONCTNTRATiOI'IS, AND STCCHI DISC DTPTHSl

Covari ance þalys'is_ for Each Test Lake

Table 11 lists the saljent features of t.he covariance analyses for the

lThe stati st'ical ana'ìyses v¡ere conducted by John t{. l^li I ki nson , Ph. D. , Renssel aer

Polytechnic Institute, Troy, N.Y.

-60 -

lable 1I. &variance analysis, Site 1, i,¡tCividual test l.akes

InterceptI

Past-BanChange in I

wïSlope Std Error

of Slopepz (1)

vmz (2)

Rl v.¡rStd Errorof 'nII

S¡ran

Balsam

Butternut,

Elk

Erterprise

Moss

Tcr,¡nline

TPSDChI a

rPSD

ChI a

TP(:ñ

Chl a

T"SD

ch1 Ê

TPSD

ChI a

TPSD

Ch1 a

TPSDChI a

1.44.89.99

.73

.3r1.08

1.46-.011.46

1. s6.03.85

-.33.06

-.16

.15

.24

.88

.331.06

.01-.01

.26

-.04.07

-.20

.IJ

.10

.01

-.02't 1*

.30

.20

.04

.13

.03

.08

.04

-.07.22*

-.10

.L2

.08

.L7

.09

.05

.18

.10

.06:2L

.08

.051e

.L2

.06

.12

.11

.05

.1r

"08.051)

.L7-.08

.42

.61*

.53*

.24

.L7

.62't-.14

.I5

.40*

.01

1.08*.96*.95*

1.06*or*

.40r.

.52*

.221É.¿)

.24

.24

.18

.L2

.14

.2L

.14

.L7-¿J

.11

.14

.18

.22

.24

.L7

.19

.13

.14

.14

.2I

.13

.02

.01

.00

.47

.40

.05

.08

.390.1

.06

.33

.00

.44

.32

.51

EA.JJ

.63

.2L

.00

.00

.08

.00

.04-04

.05

.06

.00

.00

.15

.11

.05

.01

.42

.00

.03

.00

(1)

Q)

R¡12 represents proportion of variability explained, by relationship withreference lake.

ffi.2¡Jl represents the increase Ín the proportion of .variability erplainedduced by the ban.

.30 .02

.I2 .35

.L2 .02

the covariate

by any shift intro-

* Statistically signifÍcant at at least the 5* level.-61 -

ìogarìthms of the responses for the individual test lakes for Site 1 data.

The est'imate for the. change jn the intercept assocìated v¿ith the post-ban

period is the feature of greatest interest. 0n'ly for Elk and Townline

Lakes fon Secch'i disc depth'is this change stat'istica'lly signìficant. Part

of thjs may be attributed to the small sampìe sizes and the'large variabi-

lity, encouraging an examìnatìon of the test lakes simultaneous'ly using a

"dummy variable" approach. This anaìysis 'is described below.

Combined Covariance Analysis for All Test Lakes

l,{hen considerìng a covariance anaìysìs of all test lakes simultan-

eously, additjonal degrees of freedo¡n become available for statistical

testing punposes, gìv'ing a gneaten capabiì'ity of detecting differences.

Centajn additjonal assurnptìons are needed to use th'is method. However, an

analysjs of the residuals after fitting the model did not suggest that,

these addit"ional assun"rpt'ions lvere unreasonabl e.

Separate anaìyses were perforrned for the logarithms of Site 1 data

on.ly and for the averages of the ìogarithrns for Sjte l and Site 2 data.

The latter disp'layect sl ightly less variabil'ity than the formen and for the

sake of brev'ity and wì'¿hout loss of clarity, it is the only analysis that

ì s reported.

'lable 12 prov'ides a summary of the analys'is of variance for each

of total phosphorus (TP), Secchi dìsc depth (SD) and chlonophyìi g (Chl g),

Fon the conrected total sum of squares, the var"iabiìity was partitioned

sequentialìy into the follovring components: reference ìake, intercept

adjustment for different test lakes, adjustment of slope of reference lake

varjables for djfferent test lakes, and fìna'11y, inLercept adjustment for

H I STON -62- February ì983

Table 12: Ana'lysis of varjance

loEarithms of SÌte L

of the average of the

and 2 data.

Test

Lake Measurement S. S. D. F.Mean

SquareTest

StatÌ sti c R2 R2

Refere'nceLake

I nterceptAdjustmentfor Test

S1 opeAdjustmentfor TestLakes

InterceptAdjustmentfor Post/Pre-Ban

Resi dual

5.471.14

.85

5.435.639.66

2,26.31

?.29

.45

.461.02

8.273.49

25.37

5,471., i.4

.85

.91

.941 .61

.38

.06

.38

.064

.066

.146

.041

.017

.J25

243 .9*67. L*6,8*

22.?*55.3*12.g*

9.3*?Ã*

3 ,0*

1.63.9*r.2

TPSD

chl

TPSD

cht

a

a

1

1

1

666

656

203203203

,25.10.02

.25

.51 '

.25

.25

.10,a?

,L0.03.06

TPSD

Chl a

.t2

.04

.02

77

7

TP5Dehl .a

TP.SD

Chl a

.50

.61

.27

.60

.64

.33

.62

.68?Ë

*Stat'istically sígnificant at at least lhe 5'/" 'level.

-63-

Table 12:

Measurement S. 5. D. F.

Analysis of variance of the average of

logarìthms of Site 1 and 2 data.

Test

the

Lakeþlean

SquareTest

Statisti c R2 R2

ReferenceLak.e

I nterceptAdjustmentfor Test

SI opeAdj ustmentfor TestLakes

Intercept,Adjustmentfor PostlPre-Ban

Res'i dual

TPSD

Chl a

TPSD

chl

TPSD

chl

TPSD

Ch1 g

TPSD

Chl a

5.471.14

,85

.91

.941 .61

.38,06.38

.064

.066

.146

.041

.017

. 125

243.9*67. 1*6.8*

22.2*55.3*L2.gx

o?*3 .5*3.0*

1.63 .9*L.2

.25

.10

.42

.25

.10

.02

.50

.61

.27'a

656

77

7

a

5.471.14

.85

5.435.63I .66

2.26.31

2.29

.45

.46t.02

8.273.49

25.37

1

1

1

666

.25

.51

.?5

.60 .10

.64 .03

.33 .06

.62 ..A2

.68 .04,35 ,02

203203203

*Statistically s'igniflcant at at least lhe 5% Ïevel.

-63-

post/pre-ban effect. Another way of expressing this is that one adjusts

the total test lake nesponse variabil ity for potential relat'ionship w'ith

the correspondi ng reference l ake response and forindi vi dual test l ake di f -

ferences and then exarnines for the effect of ìmposìt'ion of the ban. Only

the Secchi disc depth measurement shorved a detectable variation betr*een the

pre- and post-ban values at a five percent level of significance. The

neaden should refer to the Methods Sectjon (Fie1d Measurernents and

Observations) for a discussìon of the use of Secch'i disc readings jn esti-

mating aìgal growths and a lake's trophic status.

Some additjonal'information of potentia'l interest Lhat can be obtained

from Table 12 is the pnoport'ion of the variabiìity expla'ined by various

groups of terms in the model. Those ane summarìzed'in Table 13.

Aìso by inspection of the colurnn under n2 in Tabìe 12, one can assess

the proportion of variability in the clal:a explained by the model, The

rnodel appeârs to do much better in this respect for total phosphorus (.62)

and Secchi disc depth (.68) than'it does for chlorophyll a (.35).

Tab'le 14 I 'i sts each test I akes ' esti rnates of the sì ope coef f Í cì ents

for the corresponding reference Jake as rvell as estir¡ates of the arnount of

shift in the model aften the ìmposit"ion of Lhe ban" The esbjmated standard

dev'iations of these estimates ane ì'isted in parenthesis. Asterisks (n) are

used to ind'icate statistjc.al sign'ificance at, at least the five percent

I evel. .

A shift associated vrith the ban was detectable at the five percent

level in onìy 4 of the 21 cases, namely for total phosphorus in tnterprise

Lake, Secchi dìsc depth'in Elk and Townline Lakes, and chlorophylì a in

Elk Lake. In two of these cases, total phosphorus for Enterprise Lake and

r,t r sc0N -64- February .l983

Table l3: Proportion of yaria-bility explained by varÌous sourcesr

Proportion of Proportísn of Totöl

source Measuremenr, vaniabil;,:å.ï-otained variabilitv

-65-

Reference LakeCova ri ate

Test LakeD'if f erences

TPSD

Chl a.

TP

SD

ehl a

0.4CI0. L50.06

0,570.79û.86

4.250,10t.02

0.350.54CI.30

Table 14: tstimates of the post/pre-ban shift and slope-coeffic'ientfor cornesponding neference lake for the a"renage of thelogarithnrs of site I and site 2 data.

SD Chl aTD

P ost/P reÀ Intercept

P ost/P re

^ Intercept

Post/Pne Sì opeI Intercept

Sì ope Sl opeLake

Swan

Bal sam

Butternut

Etk

Enterprise

Mos s

Townl i ne

-.08(.0e)

-.01(.09)

.06( .09)

-.09( .09)

.22*( .09)

-.07(.09)

-.03( .03)

.35*(.16)

.55*(.i1)

,17 -

(.11)

.18(.11)

.87*(.16)

1.05*(.11)

,65*(.17)

.05(.07)

.10( .06)

.10(.06)

.17*(.06)

.08(.06)

.11(.06)

.08*("03)

.11(.19)

Ãr*.JL

(.17)

.6 3*(.17)

.38*(.17)

1.02*(.17)

.48*(.19)

.60*(.14)

.14(.15)

-.15(.15)

.0L( .15)

,33*(.15)

.08(.1s)

-.03( ,15)

-.01)( .06)

-0. 1

(.19)

.45*( .20)

.ûg(.20)

"07( .20)

1 .04*(.23)

.25(.24)

.59*(.18)

* Stat'isticalìy sign'ificant at at least the five percent level

-66-

chlorophyll a fon tlk Lake, a posit'ive direction in the post-ban shift is

not someth'ing that could be attributable to the ban. Hence, from this ana-

1ysis, the only effect that appeêrs to be assoc'iated with the ban ìs for

Secchi disc depth. The relative magnitude',of th j's shift is approx'irnateìy

ì0 pencent, and, a'lthough statìstically significant, a question could be

ra'ised about the meanìngfulness of its significance. Again, the reader

shoul d refer to the l'lethods Section (Fìel d l4easurements and Observat'ions)

fon a discuss'ion of the accuracy of Secchi clisc readings in estimating

alga'l growth and a lake's trophic status.

The number of sl ope estimates that are stati st'ica1ìy s'ign'if i cant is an

indicator that the relatìon of the refenence lakes to the test lakes is

accountìng for a statjst'ically :ignificant

proportion of the variability.

These data wene useful 'in making the analys'is more sensit'ive. Howeven, the

amount oî vaniability nol expìained hy this relationsh'ip is 'langer st'il'1.

l'ltrJ t i v a q i,Tlg*ln a I y s i s/]u I t i. p.l g lgg¿q¡i :ott.s.

The estilnated differences for conresponding dates between post- and

pre-ban measurements and their sirnultaneous confidence intervals are best

presented graphicalìy, Figure 3 shov¿s the results for the three anaìyses.

using Site 1, and Figure 4 the r.esults for the three ana'lyses comb'in'ing

Sites L ancl 7 for test and reference lakes combined, Figures 5 and .6 pre-

sent simiìar analyses for test lakes onìy. For each responsE variable and

yean, the left curve is the lovier confidence bound, the m'iddle curve the

estirnated contrast ,/a'lue, and the n'ight curve the upper conf idence bound,

A vertical "no effect" ìine passes through zero.

It is clear fron F'igunes 3 and 4, and 5 and 6, that the ban has not

þ,lI SCON-67 - February l9B3

Chlorophyll a Secchl Olsc 0epth

rgB2

r98r

t980

- -0.s0 . .0..sû r.so -2.00 tilårrrS,oovrrrboo

2.00 -0.40 conli!|r, V.lr.B.40Contrast Vaiue

Figure 3: Estimated differences and 95% simultaneous confidence bounds,. effects of post-ban years related to pre-ban. Data areìog measurements from site l.

-68-

jjtj!\

-r-50

Total Phosphorus

I

(

ì

(

(

{

(

Phosphorus

't98t

Total.

-0.s0 0.50Contrast Value

-t.50 -0.50 0.50 t.50Contrast Value

Secchl DIsc Depth

1982

r98r

1980

-0.40 0.00 0.40Contrast Value

confidence bounds, effects ofare average of log

-t.50

Estimated differences and gS% simultaneouspost-ban years relative to pre-ban. Datameasurements, sites I and 2.

Chlorophyll g

)

t!Figure 4i

*69-

Secchl Olsc 0epth

Jí

)

t>

:

r982

Estimated differencespost-ban year effects.measurement.

Chlorophyll a

t982

r98l

t980

-2.00 -r.00 0.00 1.00

Contrast Value

and 95% simultaneous confidence bounds forAnalysis of test lakes only, ìog site I

lgBl

-0.20 0.20 0.60Contrast Value

-2.00 -r.00 0.00 1.00

Contrast Value

Total Phosphcrus

"70-

Fi gure

Secchl Dlsc DepthjTj

,

-2.80 -r.00 0.û0 1.00tontrast Value

Chiorophyll g

-2.00 -r.00 0.00 r.0ûContrast Value

-0.20 0.20 0.60Conlrast Value

1982

r98l

r980

ts82

t98t

1980

2.C0

bounds forlog geometric

Fígure 6: Estimated differences and 95% simultaneous confidence'' post-ban year effects. Anarysis of test rakes onry,mean of site I and 2 measurements.

Total Phosphorus

!/!

)

¿

i-71-

had a statisticalìy sìgnificant effect on total phosphorus, chìorophyll g,

on Secchì disc depth, aìthough the general positive nature of the estimate

for the latter for alì post-ban years may support an indicatjon of some

effect fon Secchj disc depth.

Instead of obtain'ing interval estimates at each point in time durìng

the post-ban years, naFroþ¡er intervals with the same level of confidence

are obta'inable for the means for each of the years. These are summarized

in Table 15. For total phosphorus and chlorophylì a, none of the differen-

ces between the post-ban years and the pre-ban year are statist'ically

significant. Although only one difference'is statistically s'ignificant at

the five percent level for Secch'i disc depth, all are pointing in the 'direction of Secchj disc depth being 'improved follovling the ban.

The multivariate anaìyses of these earlier sections were completeìy

redone_on data constructed from the differences of the log test lake

responses and the corresponding log.reference lake responses. Graphs of

the simultaneous confjdence intervals on the differences between post- and

pre-ban years for each point in time that was samp'led are given in

Figure 7 for Site I onìy and in Figure I for the geometric mean (GM). In

this analysis no effect of the ban is observable.' For the diffenences between test lake and correspond'ing reference lake

responses, the year average diffenences betweeen the post-ban years and the

pre-ban year vtere estimated and 95 percent simultaneous confidence ínter-

vals constructed. Those ane summanized in Table 16. Here too, no post-ban

effect is observable.

-72-}II SCON Februany ì983

Table 15: Year average d'ifferences of the post-ban years

with the pre-ban year and simultaneous 95 percent

confidence interval s (C. l. ).

Measu rement ModelC.I. Mid Po'intsm c.I.

Hal f [.li dths

Total Phosphorus

Chl orophyl I a

Secchi DiscDepth

al I 'lakes,

al I 'lakes,

test 1 akes,test I akes o

al I I akes,al I 'lakes

,test I akes,test lakes,

all 1akes,aì I I akes,test I akes,test lakes,

Site 1

GM**Site 1

GM

Site 1

GM

Site 1

GM

Site 1

GM

Site 1

GM

.081.. 101.476.086

-.058-.049- .056- .049

.131

. i34

.r37

.r42

.179

. i65

.184

.160

.046

.007

.088

.020

.t42

.155*

.156

.773

-.00i-.010-.011-.011

-.070-.075- .079-.078

.73?

.145

.752

.164

.258

.259

.377

.379 ¡

.345

.336

.470

.498

.170

.153

.2?6

.190

* Statìstica1ly

**GM stands for

significant at at

the logarithm of

ieast 5% level.

the geometric mean of Sìtes 1 and 2

-73-

Table 16: Year average diffenences of the post-ban years with thepre-ban year and 95 percent sjmultaneous confidenceintenvals C.I. for the differences between test lake andcorrespondìng neference lake datar

C.I. Mid Points c. i.Mpa spremen t Mnrtel I 9BWB2 Ha I f t^I-i rtthq _TotaiP hosphoru s

Ch'lorophyì 1 a

Secchi DiscDepth

Site 1

Gl4*.

Site 1

GM

Site 1

GN

.020

.004

.030

.039

, 192.059

.066

" 082

-.029.003

.079

.t72

.3gB

.393

.54?

.549

.282

.26?

-.009 .022 - .042-.061 '-. 020 -.098

* GM stands for the'logarithm of the geometric mean of Sites 1 and Z

-74-

Total Phosphorus Chlorophyll a Secchl 0lsc Depth

r382

-2.00 -t.00 -1.00 -0.50 -0.00 0.50Contrast Value-t.00 0.00 1.30

Contrast Value

Figure 7: Post-Ban/Pre-Ban differencesdifference of test iakes and

and 95% confidence bounds forreference 'lakes . Si te I only.

Contrast Va]ue

Total Phosphorus

-0.50 0.50Contrast Value

Chlorophyll 'a

-2.00 -r.00 0.CI0 1.00

Contrast Value

r982

r98r t98tt98t

l9B0

2.00 -0.50 -0.00Contrast Value

Figure B: Post-Ban/Pre-Ban differencesdifference of test lakes andLog-GM of sites I and 2.

and 95% confidence bounds forreference lakes.

Secchl DIsc Depth

ì

{

I

-76-

D. PHOSPHORUS LOADINGS INTO TTST LAKES

The results of calculations for runoff and runoff rates, and the land

use measurements for each lake are shown in Tables D1 through D21. The

phosphorus nutrient budgets (Tables Ð22 through D28) show the van'ious

sources of phosphorus loads to each lake and their magnitude. Separate

calculations were made to show the phosphorus budget for the case in which

phosphate detergents were in use (i.e., the actual situation in l97S), and

for the case'in which phosphate detergents wene not being used (j.e., if

the phosphate detergent ban had been in effect). The changes'in phosphorus

loading which could be attributed to a cessation of the use of phosphate

detergents, expressed aS a percentage of the.total load w'ith phosphate

detergents ìn use, are also exhibited. In reading the tables it is helpfuì

to note that on'ly the wastewater treatment pìant and septìc tank'loadings

were affected by detergent phosphates.

HI SC0N

-77 -February .l983

A.

V. DISCUSSION

PHOSPHORUS LOADS AND THT EFFECTS OF DETERGF:NT PHOSPHt)RUS ON THE TROPHIC

When considering the importance of detergent phosphorus, ìt should be remember'ed

that detergent phosphorus represents 30 percent, or 1ess, of the total phosphorus

concentration in untreated, domestjc wastelvater. Another factor to be considered,

especially for Enterprise and Moss Lakes,'is that many of the dwellings w'ith sept'ic

tanks probably do not have laundry facil"ities or other modern appììances, thereby

reclucing the 'impact of detergent phosphates as a nutrient source.

In 1978, the reduction in the year'ly phos'phorus loadings to the test lakes due to a

phosphate detergent ban is estimated to have been less than 7 percent of the total

loads, with the exception of Swan Lake where a reduction of 12 percent was estimatecl to

have occurred (fa¡l es 022-D?8 and Table 17). The princìpal reason for the reiative

ins'ign'ificance of phosphorus originating from phosphate detergents was the large,

non-point loadings attributable to the trjbutaries and runoff from the direct drainage

areas of the I akes

t¡lhen caiculations of actual loadings w'ith and without the presence of detergent

þhosphates are compared to the loading criteria proposed by Vollenweider (1975), it Ís

readily seen that the removal of phosphorus from detergents woujd not have any

significant effect on the troph'ic status of the lakes (Table 18 and Appendix H). hlith

the exception of tnterprise and Moss Lakes, reductions in the total -vearly phosphorus

loads of 69 to 86 percent would be requ'ired to attain Vollenweider's "permiss'ible".loading rate and none would meet Vollenweider's critical criterÍon even if 100 percent

removal of phosphorus was attainecl at the wastewater treatment plants and in septic

tank/tile fjeld systens. Therefore, even a compiete el'imination of l,ll'lTP and septic tank

phosphorus loads to these lakes would not be sufficjent to meet Vollenweider's "per-

missible" load'ing rates

-78-

Table 17:, Total phosphorus loadíngs to test lakes due to vastevater andphosphate detergents.

Lgl"1e , ., C,oul'lty Wastevater ,,, Phosphate DeterqentsBa I sâm Lake Hashburn <1

Pereent of Curre¡ttPhosphorus LoadAùtributable to

?3(a)

22

13

19

tlO( a )

12

Percent of CurrentPhosÞhorus LOådA¿t.ributab¡e to

6

12

4

Butternut Lake

EI K LâI(e

gnterpri åe Lske

MoEs LâKe

SVan Lâhe

Townl ine Lake

Príce

PFiCE

Lang I åde

Vi lâs

Columbia

One i da

(alt lmBlementatíon of phospnorus removal îs plaRned.

-79-

Table 1B: Compa r i son of theof Vol lenweiderts

Ba I samlakedet P.

\,/¡th v/o

actua I 1978 I oad i ng of11975, permissible and

phosphorus to the test lakescritícal loading valué.

to ca I cu I ated va I ues

Butte rnutLa kedet P

w¡th w/a

EtkLã ke

EnterpriseLâ ke

Town I i neLa kedet P

wíth vlodet P

v¡th v/o v¡t,h v/o with v/o

r1võ-iRês i

T ime

aulicdence 0. 17 0.50 o. 004 r .09 2.OB 0. 36 0.61lvrì

Actrral Load (a)(g/sq n/yr) 3.00 3.00 0.62 o.57 21.2 19.9 O.1L¡ û. 13 0. 08 0,08 2.7U 2.42 1.09 1.ol.l

Pe rm í ss i b I eLoa d( g,rsq m/Yr)

criticalLoa d(s/sq m/yr)

o. 58

1.16

0. 19

0. 37

3. B5

7.74

0. 14

o.27

, 0.12

o.23

0. 37

o. 74

0. 16

0. 31

/o Reduct ionin 1978 LoadReqtr i red toReach thePermissibleLoad.

B5B68?6981

(a): A loâdir¡g lesscrit¡cal values

than the permissiblea mesotroph ic iake,

vâlue suEgests anand greater than

ol igotrophic lake,the cr¡tícãl value

between thea eut,roph ic

permlssible ãndlake.

-80-

Nutrjent enrjchment limìtation bjoassays provided additiona.l evidence that even

ìarge reductions in phosphorus loads to Swan Lake might not result in observable

improvements in water quality. In Swan Lake water, both phosphorus and nitrogen

enrjchment was requ'ired for algaì growth stimula'Ljon to be observed in August. The

mid-August bjoassa¡r results were supported by chìorophyll a, analyses and algal counts crf

lake water samples which suggestecl that a1ga1 growth did not occur during at least the

first half of August, 1982.

For Townline Lake, the nutrient enrichment bioassays indicated that n'itrogen was

required for increased algaì biomass'in early August,7982, and phosphorus or nitrogen

was requ'ired in mid-August. The chjorophy'I1 a analyses and algal cell counts supported

these results showjng a decline in chlorophyll a concentrations and cell numbers

starting in early August. Neither orthophosphate nor total dissolved phosphorus

analyses were conducted routinely in 1982, but the filtered peak productivity samples

collected on July 2i and August 4 v¡ere analyzed for total dissolved phosphorus (Tnp) and

total soluble inorganìc nìtrogen (fSin, i.e. nitrate, nitrìte, and ammonia n'itrogen).

Although N:P ratìos are usually calculated as the ratjo of TSII'l to orthophosphate, the

TSIN:TDP ratio which can be calculated from the available Townline Lake data can aiso be

instructive. The TSIN and TDP concentrations'on Juìy 21 were 28 ug N/L and 4 ug P/1,

yielding a TSIN:TDP rat'io of 7:1; the concentrations on August 4 were less than 60 ug

N/L and 48.ug P/L providing N:P ratio of less than 2:1. Simjiar observations were made

during the NES study. Such low levels of total soluble inorganic nitrogen relative to

totaì djssolved phosphorus are h'igh1y suggestive of nitrogen limitation. These

observations could expìain why Townline Lake has not experienced major water quafity

problems although Vollenweider's phosphorus loading criterìa calculations would

categorize Townline Lake as eutrophìc. A reduction in the total phosphorus loadíng by 4

percent could not be expected to have a major effect on this Lake.

-81-

Algal growth was stjmulated by phosphorus additions to Balsam Lake water on all

bioassay dates. Therefore, a reduction'in phosphorus in July and August rnight reduce

the aìgal bíomass. However, the phosphorus nutrient budget for 1978 showed detergent

phosphorus accounted for less than 1 percent of the total load. Due to the very small

reduction in phosphorus loads whjch would occur as a result of a detergent phosphorus

ban, n0 observable effect would be expected.

Regarding hyrJraulic residence time, the situation at Elk Lake was different than

expected from the data available prior to the study" The hydraulic residence time of

the lake was found to be less than five da.vs. Thjs rapid turnover of lake v¡ater creates

conditions under whjch a large, relatìveìy constant supplv of phosphorus is entering the

lake; the mean total phosphonrs concentrations in the in'let during 1981 and 1982 were

0.054 and 0.057 mg P/1, respectively, and the mean orthophosphate concentration was

0.015 mg P/L in i981. The nutrient enrichment b'ioassays indica'ted stjmulation rvith both

nitrogen and phosphorus was necessary to i ncrease a'l ga'ì b j ornass i n mi d-Juìy, but

phosphorus additions alone stimulated aìga'l growth throughout August. Silicate also

yieided jncreased standing crops'in mid-Ju'ly and mid-August; this is an important

observation since diatoms, which require appreciable quantities of silicate, were an

important component of the algal comnrunjty in Elk Lake. Due to the rapid flushing of

the lake, constant replenjshment of phosphorus from the in'let, and possible si'licate

limitat'ion, detergent phosphorus would not be expected to have a signìficant effect on

the trophic status of Elk Lake.

Butternut Lake showed that phosphorus stimulated a'lgaì growth in August and,

therefore, a reduction in the a'lga1 stand'ing crop mìght result from a reduction jn the

phosphorus loads during those periods. However, as ev'idenced by Voìlenweider's (19i5)

loading criterja, the improvement due to the removal of detergent phosphorus would not

be sjgnificant (7 percent) and the iake would remain in a eutrophic state.

-82-

B.

Both Enterprise Lake and l'4oss Lake had phosphorus loadings vrith'in Vollenweider's

permissible range, suggesting ol igotrophic conditions. Detergent phosphorus accounted2for 0.01 g p/n,/yr,0r'less, in both these lakes, a quantity of questionable importance

relative to the total ìoad'ings (0.14 g p¡*?'/y, at Enterprise and 0.08 g P/m2/vr at

Moss). S1Íght water qua'lit.y irnprovements rnight ûccur at Enterprise Lake sjnce

phosphorus was shown to stimulate algal grolth in the August nutrjent bioassays.

In Moss Lake water collected in Auqust, increases in a1gal biomass occurred on'ly when

both phosphorus and n'itrogen were added. Moss Lake chlorophyll a concentratjons were

consistently low throughout the study. Therefore little, if any, change in trophic

status could be expecteci at tnterprise and I'loss Lakes due to the removal of nhosphorus

from detergents.

E|rL TTY PARAMTTERS

TOTAL PHOSPHORUS, CHLOROPHYLL A AND STCCHI DISC DTPTH

The employment of reference lakes having negligibìe infìuence from wast.ewater was

useful in explainìng some of the natural variabiiity in the test lake data. llovrever,

the magnìtudes of the amounts of the variability exp'lained were smal1, ranging from 25

percent for total phosphorus to 2 percent for chlorophy'll a.

All the ana'lyses performed are consistent in their indication of a statistical'ly

sìgnificant shift ìn Secchi dìsc depth assoc'iated w"ith improved water clarity after the

ban. The estimated magnitude of this shift is reasonably consistent across the test

lakes. The detectability of the shift, statisticalìy, was aidecl by the ap¡:arent smaller

relative variability of the Secchi djsc measurements. This could be spurious due to

inherent errors'in Secchi disc measurements (see the Methods Sect'ion for a discussion of

this subject). These possibif itjes need to be recognized 'in interpreting the

meaningfulness of the apparent Secchi d'isc depth shift.

-83-

For example, the expectecl inverse relationship between Secchi disc depth and

chlorophyì1 a appears to have been lacking ìn Townljne Lake in 1978 (Figure F1). In

this lake, one of two study lakes exhibiting an improvernent in Secchi d'isc depth

measurements between the pre- and ban periods, the expected relatjonship between the two

variables'is more observable in the ban period 1980-BZ (Figures F2, F3 and F4), though

many data points appear to be inconsistent. Sim'ilarly, jn 1981, Elk Lake unexpectedly

exhibjted a direct Jinear relatìonship between Secchi d'isc depth measurements and

ch'lorophyll a analyses (Figure F7). In 1980 no relationship appears to have existed

between the two parameter (Fìgure F6). 0n1y in 1978 and 1982 djd Secch'i djsc depth

measurements appear to vary'inversely with chl.orophyll a concentrations in tlk Lake

(Figures F5 and FB).

In view of'uhe lack of the inverse relationship between Secchi disc depth and

chlorophyll a jn these two lakes during.certain years of the study, it can be concluded

that factors other than a'lgaì concentrations, as measured by chìorophyl"l jr, are

affecting water c'larity (j.e., suspended solids concentrations and sizes, natural

coloration surface'light intensity). Since these latter factors are unaffected by lake

phosphorus concentrations and, therefore, detergent phosphorus, a more direct measure of

the ban's effects is through ana'lysis of total phosphorus and chìorophyl'l a

concentrations ìn the lakes. Whether ana'lyzed'individually or as a group, the test lakes

did not exh'ibit any statistical'ly signìficant improvements in either lake total

phosphorus concentration or chlorophyll a concentratjon.

The analysis using multivariate methods that took into account the potential

covariances among the data generated inferences cons'istent with those obtajned from the

covariance analyses. This is grat'ify'ing in that it makes one more confident of

insights that have been possible from examin'ing the covariance mode. This is l'ikeìy

attributable to the fact that the magnitudes of the correlations in the data over time

-84-

turned out not to be large relative to the inherent variability encountered for the

sample sjzes availabie. Alsoo ali analyses were performed on the logarithms to the base

10 of the orig'ina1 data. Subsequent residual analys'is supported the reasona.bleness of

usìng this scale and assuming that the resultìng dìstribut'ion of the transformed

measurements could be approximated by a Gaussian distribution.

The ìnherent variabiìity'in the data stemming from measurement and sampling

variabil'ity combined was estjmated foÈ total phosphorus and Secchi dìsc depth to be

suffic'ientìy great such that a sh'ift, or change, of approximateìy L0 percent v¡ould be

needed to bp able to detect a shjft at the 5 percent'level of signifìcance. An even

higher percent shift 'in chlorophy'll t wou'ld be needed for detection with current

variabi'lity estimates. If the magn'itudes of the shifts, turn out to be smaljer than

this, then their potential detection will requ"iìe more data or improved models or both.

it can be inferred from th'is that changes in water quality that occur as a resuit of

phosphorus load changes less than L0 percent are impercept'ible to the scient'ist

utjì'iz'ing a reasonable monitoring program.

C. STATISTICAL ANALYSIS OF TEMPORAL VARIATIONS IN GRETN AND BLUE GRETN ALGAL COUNTS1

If a nutrient, such as phosphorus, is the. factor controlling aigal productivity in

lakes, one would expect to observe a decrease in alga1 counts (biomass) if the

phosphorus supp'ly is reduced sign'ificantly. Figures GlA through E and G2A through E

(Appendix G) clear'ly show there was a continual increase in both green and blue-green

algaì counts, respectively, throughout the study period and in all lakes. The monthly

means of the counts are plotted.

A statistjcal anaìys'is of these data confirms that no reductions in b'lue-green or

green a'lgal counts occurred in the test lakes relatìve to the reference lakes as a

result of the ban. Analyses were conducted on logarithm. of blue greens (ln BG),

logarìthm. of greens (1n G), p = BG/(BG+G), and 1n [p/(l-p)]. The transformations,

where used, were for obtaining better agreement w'ith the distributional assumptions for

lThe stati sti cal ana'lysi s vras

Polytechnic institute, Troyo

conducted by John bl. l,lilkinson, Ph. D., Rensselaer

New York

-85 -

the various analyses. The use of the logistic transformation, ln P/(l-p), v¡as of

margìna'l value.

Tabies Gl and G2 represent covaríance analyses s'im'!jar to those done for total

phosphoruso chlorophy'll a, and Secchi disc depth. For all rneasurements considered, the

apparênt tracing of the test lakes by the reference lakes is accounting for a

substantial amount of the total variabi'l'ity (Table G1). Even so, except for the greens,

the post-ban effect js statistically sign'ificant (although not dramat'ically so). This

post-ban effect is primariìy associated with ilk Lake, with Butternut also appearing for

the blue greens (Table G2). In both instances, the direction'is associated v¡ith

increases in the blue greens that were greater: than corresponding reference lakes.

Although the causal factor(s) for these increases is not clear, the data do not support

the hypothesìs that a phosphate detergent ban would result in decreases ìn algaì

b'i omas s

Another poss'ible indicator of general trends in lake water qua'lity uses green and

blue-green aìgae and the proport'ions of each in a lake's aìgal cornmunity" Genera'lìy, as

water quaìity inrproves and the amounts of nutrients decrease, one might expect an

overa'11 shift in the aìgaì commun'ity structure. wjth green algae increasjng Ín 'importance

relatjve to blue-green aìgae. These changes must be monitored over a period of years,

and should not be assocjated with the normal seasonal changes occurring over the course

of a single year. From the stat'istical analysis (taUles Gl. and G2) it is apparent that

such a shift in the proportion of the two alga1 types did not occur as a resu'lt of the

phosphate detergent ban, suggesting s'ignificant water quality 'improvements did not

occur.

D. PHOSPHORUS RESIDENCE TIME AND LAKE RTSPONSË

As an area

phosphorus has

of investigation, the exact

received only limited study.

nature of the internal recycling of

Yet, a mathemat'ical approach to the

-86-

solution of the ultimate concentration of phosphorus in a lake in response to an ínput

or change Ín input of that element offers some ins'ight. As an a'lternatìve, one rxay

calculate the length of tjme it would take to achieve the ultimate concentration given

that change ìn input.

The development of such a mathematical model is described by Sonzogni et al.

(1976). The basis for the modei is equating a lake to a completeiy mixed reactor with

constant chemical influx. Factors are then included'Lo account for internal losses such

as sedimentation (k) and stratifÍcation (c). Phosphorus residence time is used rather

than hydraulic resìdence time sjnce phosphorus is a nonconservative element.

The basic

'frwhere:

equation ìs therefore:

= Q^. - Q c - kVcu'l a

! = volume of the lake (t')

a = volumetric flow rate (l3r-1)

c = concentration in the lake (l¡t--3)

ci = constant influx concentration (ml-3)1

k - internal loss rate constant (T-')

= dimensionless proport'ionality factor thatrelates the mean annual outwash or surfacewater concentration to the mean annual con-centration over the whole iake.

After substitutions and rearrangements, the equation can be expressed'in terms of

the ultimate steady-state concentration as:

= 6-t/RO

-87 -

where: R^ = phosphorus residence timep

=VQa+kV

f, = time

C^ = lake concentration before the step change in influxo

C = concentration Ín lake

C* = ultimate lake concentration after a step change in influx

. According to Sonzogni et al. the time required to reach 95 percent of the expected

change wil'l be a time perìod equal to three phosphorus residence times. Estimates of

the phosphorus residence times forr the study 1akes, calculated as the quotient of the

mean annual content and annual input of phosphorus ín 1978, are presented in Table 19.

These data indicate that 95 percent of the expected change should have been observable

in all the test lakes by the end of the ban.

-88-

Tabie 19: Number of Phosphorus andand percent of expected

hydraulìc residence times during banchange that should be observable.

Yearly Mean [Total P] from1978 volume propor-

tionai samples (mq/L)(a)

NumberofP

Res i denceTimes

Phosphorus BetweenResidence 7 /I/79

Time andPercent

of

Hydraul i cResi dence

Time

Number ofHydrauì i cRes'idence

TimesBetween

7 /117eand

7 /1/82(Yr:) 7 /1/BZ Response (Yr)

Bal sam

Butternut

Etk

Enterpri se

Ì4oss

Swan

Townl i ne

0 .061

0 .071

4.077

0.024

0 .023

0.112

0.0s6

0.17 18

0.49 6

0.00s 600

0.65 s

0.87 3

0.40 I0.17 18

( 100%)

( 1oo% )

( ioo%)

(ee%)

(e5%)

( 1oo%)

( 100%

0. i8

0.52

0.004

1.48

2.49

0.39

0.61

17

6

754

2

2

I5

(a) Caiculated as the lakeconcentration) divided

phosphorus content (volumeby the phosphorus loading

times mean yearìy(from Appendix D).

-89-

3.

CONCLUS IONS

1. After a three-year time span without detergent phosphorus in wastewaters,

the test lakes did not show any changes in chlorophyll a or total phosphate

concentration attributable to the ban.

2. }{hile statistical analysis indjcated a statisticalÌy significant shift in

Secch'i disc depth assocíated'p'ith ìmproved water clarity after the ban, this

shift is inconsistent w'ith the trends in cho'rophylt g and totaj phosphate

concentrations. This indicates that other factors (e.g. suspendeci solids,

color) were affectìng the Secchi disc depth readings.

Nutrient enrichment bioassays demonstrated the importance of phosphorus and

nitrogen in the nutrient dynamics of the test lakes, particularly as the

surmer season progressed.

The dominance of blue-green algae in the phytoplankton has been on the

increase since 1978'in both the reference lakes and the test lakes. This

occurrence is obviously unrelated to a detergent phosphate ban, indjcating

the importance of other factors (chemical, physical or biological) as regu-

lating the ecosystem dynamics in these lakes.

5. Utilizing phosphorus 'loading estimation technìques, the total amount of

phosphorus entering the test lakes from all sources was reduced by 0.1 to l1

percent as a resul t of the ban

6. Non-point sources of phosphorus (those not derived from wastewaters) were the

dominant loadings in the test lakes.

¿.

-90-

7. Treated wastewater discharges to the soil rather than to a lake or one of

i ts tri butari es prevents the wastewat.elimpacts normal ly encountered 'in

di rect dì scharges.

t¡I sc0N :91 - February l983

V I I. REFIRENCES

Alberts, t.E,, G.E. Schunan, and R.E. Burweì.l, 1978. Seasonal runofflosses of nitrogen and phosphorus from Hissouni Vaìley loesswatersheds. J. Environ, Qual. 7:203-208.

A.P.H.A., 1975, Standand l'lethods for the Exam'ination of Hater andl,lastewaten. I5th ed. , A¡neri can Publ i c Heal th Associ ati on, New York ,lì93 pp.

Be1l, J.M. and A. Spacie, March 20, 1978. Trophic. Status of F'ifteenIndiana Lakes in 1977, Purdue Unì vers'ity.

Berman, T., 1970, Alkaline phosphatases and phosphorus ava'ilabiìity inLake Kinneret. Limnol. Oceanogr. , 15:663-674,

Bortleson, G.C., 1970. The Chemical Investigation of Recent Lake Sedimentsfrom l,liscc¡nsin Lakes and The'ir^ Interpretation. Ph.D. Thesis,University of l,l'isconsin, Madison.

Carlson, R.E., 1980. Mone complìcat'ions 'in the chìorophyl l-Secchi discrelationship. Limnol. 0ceanogr., 25:379-382

Chapra, S.C., 1982. A budget model accountìng for the pos'itionalavailabil ity of phosphorus 'in lakes. Hater Research, 16:205-209.

Chapra, S. C. and R. H. Reckow , 1979. Expressi ng the phosphorus 'load'ing

concept in probabilistjc terms. J. Fish. Res. Board of Canada,36:?25-??9.

Chen, C.T,J., 1970. Concepts and utilities of ecological models. J. San.Eng. Djv. ASCE, 96:1085.

Clesceri, N., 1981. The Impact of Banning Phosphate-Conta'ining Detengentson the !'later Qual'ity of l,lisconsin Lakes - Januany,

.l982. Report tothe Soap and Detergent Associatìon, N.Y. 56 p.

Clesceri, N.1., and G.F. Lee, 1965. Hydrolysis of condensed phosphates-I:non-stenile environment. Int. J. Air l.lat. Poll., 9:723-742.

Cowen, l.l.F., and G.F. Lee, 1976. Phosphonus avaiìability in panticulatematerials transported by urban runoff. l.Iater Poll. ControlFed., 48:580-591.

DePinto, J.V. , 1982. Techn'ica'l note: an experìmental apparatus foneval uati ng kì net,'ics of ava'il abl e phosphorus rel ease f rom aquati cparticulates. Waten Research, 16:1065-1070.

l.tI scON -92- Februany ì983

DePinto, J.V., T.C. Young, and S.C. Mart'in, 1982. Aquatic sediments.J. Hater Poll, Control Fed., 54:855-862.

DePinto, J.V., T.C. Young, and S.C. Martin, 1981. A'lga'l-ava'ilablephosphorus in suspended sed'iments from lot,ren great lakes tributaries.J. Great Lakes Res., 7:3ll-325.

DePinto, J.V., J.K. tdzwaìd, M.S. Sw'itzenbaurn, and T.C. Young, 1980.Phosphorus Removal in Lower Great Lakes Mun'icipa'l Treatment Plants.USEPA, EPA-60û/Z-80-117, Municipa] Environmental Research Lab,0f f. R&0, Cinci nnat'i, Ohio, L47 p.

D'ilìon, P.J. and I'1.8. Kirchner, 1975. The effects of geo'logy and ïand useon the export of phosphonus from watersheds. Water Research,9 :135-148.

Diì'lon, P. J. and F. H. Rìgìer, 1975" A simple method for predicting thecapacity of a lake for development based on lake trophic stauus. J.Fi sh. Res. Board Canada , 3?:l 5l 9-l 53ì.

Dilìon, P.J., and F.H. Rigler, I974" The phosphorus-chlorophyllrelationships in lakes. Limnol Oceanogr.,19:767-773 (from Jones andLee, 1982. l.Jater Reseanch 16:503-515) .

Dorich, R.A., D,ì,{. Neìson, and L.E. Somrers, 1980. Aìgaì ava'ilability ofsediment phosphorus in drainage water of the black creek watershed.J. Env. Qual., 9:557-563.

Downes, M.F., and H.H. Paerl, 1978. Separation of two dissolved reaciivephosphorus fractions in lake water. J. Fish. Res. Board Can.,35 :1636- 1639.

Edmondson, l,l.T. , 1980. Secchi di sk and chì orophy'l'1. Limnol . 0ceanogr. ,25:378-379.

Engelbrecht, R.S., and J.J. Morgan, 1959. StudÍes on the occurrence anddegradation of condensed phosphate in sunface watens. Sewage Ind.Wastes, 3L:458-478.

Environmental Protectìon Agency, 1971. Alga'l Assay Procedure Bottle Test.Nat'ional Eutrophication Research Program, USEPA, 82 p.

EPA, undated. "Effects of a Phosphate Detergent Ban on llìsconsin Waters."USEPA-Convallis Environmental Research Labonatory, Corvallis, 0regon.

EPA, 1979, Hethods for Chemical Analys'is of l.Jater and l'Iastes, EPA,E PA- 500/4 -7 9-020 .

Etzel, J.t., J.M. Beì.l, E.G. Lindermann, and C.J. Lanceìot, 1975a.Detergent phosphate ban yields little phosphonus reduct'ion, Par^t I..J. Hater and Sew. l.lorks, 122: (9)91-93.

hII SCON -93- February 1983

Etzel, J.E., J.M. Beì.ì, t.G. L'indermann, and C.J. Lancelot, 1975b.Detergent phosphate ban yìeìds l'ittle phosphorus reduction, Part II.J" Hater and Sew. Works, I22z(10)91-93.

Etzel , J.E., J.M. Be'11, E.G. Linder"mann, and C.J. Lancelot, 1975c.Detergent phosphate ban yields l'ittle phosphorus reduction, Part III.J. Hater and Sew. l{orks , 1?22 (11)68-70.

Fitzgera'td, G. P., 1970. Aerobic lake muds for the rernoval of phosphonusfrom lake waters. Limnol. 0ceanogr. -] 3:550-555.

Fitzgera'ld, G.P., and T.C. Neìson, 1966. Extractive and enzymat'ic anaìysisfor limitjng or surp'lus phosphorus in aìgae. J. Phycol.,2:32-37.

Goldman, C.R., 1965. Hicronutrient limiting factors and their detection ìnnatural phytoplankton populations, Hemonie Ital. Inst. Idrobio'1.,Suppl., 19-:121

Hanins, L.L., J.N. Dornbush, and J.R. Andersen'' !974. Physical andchemical quality of agrìcuìtural land runoff . J. l,later Poll. ControlFed., 46(i1) :?460-2470.

Hasler, 4.D., I974. Eutrophication of lakes by donrestic sevrage. Ecology,28:383.

Hutch'ins0n, G.E., 1973. Eutroph'icat'ion. Amer'. Scientist, 61 :269-279.Ip, S.Y., J.S. Bridger, C.T. Chin, l.l.R.B. Martin and !l:6.C. Raper,1982. Aìgaì growth in prirnary settìed sewage: The effects of five keyvariables. l{aten Research, 1626?!-632.

Hutch'inson, G,E., 1957. A Treatise on Limnology. I. Geography, Physics,and Chemistry. New York: John Hììey and Sons, Inc.

Jenkins, D., l,l.J. Kaufman, P.H. l'lcGauhey, A¡J. Horne, and J. Gassnen, 1973.Envi ronmental 'impact of detengent bui I ds in Caf iforni a waters. l,laterResearch, 7:265-281.

Jones, R.4., and G.F. Lee, 1982. Recent advances in assessing impact of' phosphorus 'loads on eutrophication-related water quality. WaterRe sea rch , 1 6 : 5 03- 5 1 5.

Karl-Kroupa, 8., C.F. Callis, and E. Seifter, 1957. Stability of condensedphosphates in very dilut,e solutions. Ind. Engng. Chem. 49:2061 -2062.

Kluesenen, J.l^l., and G.F. Lee, 1974. Nutrient loading from a separatestorm sewer in Madison, l.lìsconsin. J. Water Poll. Control Fed.,46(5):e20-e36.

Landon, R.J., 7977. Characterization of Urban Stonmwaten Runoff in theTri -County Regi on. 208 T,later Qual i ty Managernent Pl an. M'ich'igan

. Tri -County Regì onaì Pl anni ng Comm'i ss'i on , 136 pp.

IilI SCON -94- February l9B3

Langowska, I., 1982. Ut'ilization of organ'ic phosphates by selectedbacteria and aì gae. Water Research, 16:161-167. .

Larsen, D.P. and H.T. Merc'ier, 1976. Phosphorus retention capacity oilakes. J. F'ish. Bd. Can., 33:1742-1750.

Lean, D.R.S., 1973a. Movernents of phosphorus between'its bio'logica'l'ly, important forms in lake water. J. Fish. Res. Board Can.,

30:1 525-1 536.

Lean, D.R.S., 1973b. Phosphorus dynamics in lake water. Science,179:678-680.

Lewin, V. H., 1973. Phosphates in sewage treatment. Hater Research7 :55-67.

Lee, G. F., R. A. Jones, and H. Rast, l98û. Availability of phosphorus tophytop'lankton and its imp'lì cations for phosphorus management strate^gies, pp. 259-308. In: Phosphorus Management Strategies for Lakes,Loehr, R. C., C. S. Martin, and l,i. Rast (eds. ), Ann Arbor SciencePubl., Ann Anbor, MI.

Leen G.F., 1973. Role of phosphorus in eutrophication and diffuse sourcecontrol. Hater Research, 7:111-128,

Likens, G.E.,1974. Water and Nutrient Budgets fon Cayuga Lake, New York.Cornelì Univ., l,Jater Resources., Mar, Sci. Center. Tech, Rep., 82.p. 91.

Lorenzen, M.H., 1980. Use of ch'lorophyll-Secchi disk relat'ionships.Limnol. 0ceanogn., 25:37I-37?.

Megard, R.0., J.C. Settìes, H.A. Boyer, and H.S. Combs, Jr., 1980. Light,Secchi di sks, and trophi c states. Limnol . Oceanogr. , .25 :373-371 .

Morrison, D. F.,1976. Multivaniate Statjstical Methods, (Chapter 5).l,liley, N.y.

l,lortimen, C. H., 197.|. Chemicaì exchanges between sediments and waten inthe Great Lakes - specuìations on probable regu'latory mechanisms.Limnol. Oceanogr. lg:387-404.

l,îortimen, C. H., 1942. The exchange of dissolved substances between mudand water in lakes (Parts III, IV, summary, and references). J. Ecol.30:147-201.

Mortimer, C. H,, 1941. The exchange of dissolved substances between mudand water in lakes (Parts I and II), J. Ecol. 29:280-329.

Middlebrooks, E.J. and D.B. Porceìla, 1970. Rational multivariate algalgrowth kinetics, technical note. J. San. Eng. D'iv., Amer. Soc. CivìlEng. , 97:133.

Mumma, C. E., F. C. Hopkins, K. Bohannon, and T. hl. Lapp, lg7g. Analysis of theSources of Phosphorus 'in the tnv'ironment. tPA-560/2.-79-002. Mai'ch 1979.

-95-

Murphy, J., and J.P. Rì1ey,1962. A modìfied singìe solut'ion method forthe detenmination of phosphate in natural watens. Anal. Chim. Acta,27 -.3I-36.

NtS, 1974a. Report on Butternut Lake, Ashland and Prìce Counties,l{iscons'in. þlonk'ing Paper 1134, U.S. EPA, National EutrophìcationSurvey,26 pp.

NES, .l974b. Report on Swan Lakeo Col unibi a County, l*lì sconsi n, llorki ngPaper #5û, U.S. tPA, National Eutrophication Survey, 24 pp.

NES, 1974c. Repor"t, on Townl ine Lake, Oneida County, Hisconsin. tlorkingPaper #53, U.S. tPA, Nat'ional tutrophication Survey, 23 pp.

0akes, E.L. and R.D. Cotter, 1975. Hater Resounces of l{'iscons'in-Upperl-li sconsi n Ri ver Basi n Hydrol ogí c Investi gati ons At'las, HA-536.U.S.G.S.3 pp.

0gìesby, R.F., and l^I.R. Schaffner, 1978. Phosphorus loadings to ìakes andsome of theì r nesponses. Part 2. Regne'ssì on nodel s of summerphytopìankton standing crops, winter total P, and transparency of New

. York lakes with known phosphor"us ìoadings. Limnol. Oceanogn.,23: 1 35- 145.

0lcott, D.G., 1968. Haten Resources of Hisconsin Fox-þlolf River BasinHydroìogic Invest'igations Atlas, HA-321, U.S.G.S., 4 pp.

Paerl, H.1^l., and M.F. Downes, 1978. Bio'logica'l availab'ility of lovr vensushigh molecular weìght react'ive phosphorus. J. Fish. Res. Board Can.,31:1639-1 643.

Perry, R., J. N. Lesler, R. M. Harrison, and V. Lewin, 1975. The balanceof heavy metals through a sewage treatment process. Pnoceedìngs ofthe Intennational Conference on Heavy I'Tetal s in the Envi ronment,Toronto, pp 453-461.

Peters, R.H., I979. Concentrations and kinet'ics of phosphorus fractionsalong the troph'ic gradient of Lake Memphremagog, J. Fish. Res, BoardCan., 36:970-979.

Peters, R.H., 1.978. Concentrations and kìnetics of phosphorus fractions inwater f rom streams enteri ng Lake Mernphnernagog. J. Fi sh. Res. BoardCan,, 35:315-328.

Peters, R.H. , !977 . Ava'i I abi I 'ity of atmospheri c orthophosphate. J. Fi sh.Res. Board Can,, 34:918-924.

Pitcairn, C., and H.A. Hawkes,1973. The role of phosphorus in the growthof Cl adophona. l.later Research, 7:159-171.

Poncella, D.B. and A.B, Bishop, 1975. Comprehensive Management ofPhosphorus l.later Pol'lut'ion. Ann Arbor Sc j ence, Ann Anbor, l4I.

hII SCON -r, ;96- February ì983

Rast, hl. and G.F. Lee, 1978. Summary Ana'lysis of the l'{orth Arnenican (U.S.port'ion) 0ECD Eutrophicat'ion Proiect: Nr¡trient Loading -- LakeResponse Relationshjps and Trophic State Indìces. EPA 600/3-78-008,U.S. EPA, Corval 1 is, 0R.

Reckhow, K.H. , H.N. Beauì ac, and J.F. S'impson, 1980. Model'ing PhosphorusLoading and Lake Response Under Uncertainty: A l4anual and Compìlationof Expont Coeff ìcients. tPA-Off ice of l,later Regulat jons andStandards, EPA 440/5-80-011, 2ì4 pp.

Richey, J.E. 1979. Patterns of phosphorus supply and utilÍzation in Lakel,iashi ngton and L'ind'ley Lake. Limnol . Oceanogr. 24:906-916.

R'ichey, J.8., 1977. A mathematical approach toward the development of a

phosphonus model of Castle Lake, Ca'lifornia, p. 268-287. .In: C.A.Hall and J.l^1. Day, JF. (eds, ) Ecosystem Model'ing ìn Theoryi-ndPract'ice: An Introduct'ion with Case llistories. l,li1ey.

Runke, H.14", 1982. Ef fects of Detergent Phosphorus on Lake 'vlater Qual ityin l"linnesota: A Limnologica'ì Invest'igation of Representative MinnesotaLakes 1975-1980. tnvinonmental Research Group, Inc., St. Paul, MN.

Sawyer, C.N.,.l952. Some new aspects of phosphates in relation to lakef erti ì'izati on. Sewage Ind. l^lastes ?4:768-716.

Sawyer, C.N., 1947. Fert'ilization of lakes by agricultural and unbandra'inage. Jour. New Engìand Haterworks Assoc. 6l:109-127.

Schaf f ner", l^l. R. , and R.T. 0gì esby, 1978. Phosphorus I oad'i ngs to I akes andsome of thein responses, Part I. A new calculation of phosphorusloading and 'its application to 13 New York lakes. Limnol. Oceanogr.,23:120-134.

Schindìer, D.l^l. and J,E. Nighswanden, 1970. Nutrient suppìy and primaryproduction in Clear Lake, Eastern 0ntario. J. Fish. Res. Bd. Canada,27:2009-2436"

Schuman, G.E., R.G. Sporner, and R.F. Piest, 1973. Phosphorus losses fromfoun agr''icultural watersheds on Missouri Va'lìey 'loess. Soil Sci. Soc.Amer. Proc. , 37:424-427.

Singen, M.J. and R.H. Rust, 1975. Phosphorus in surface runoff from adecid'ious forest. J. Envi ron. Quality, 4(3):307-311.

Soap and Detergent Associ ati on, 1982. ï,li scons'i n Lakes Study, 1982:Protocol. The Soap and Detergent Assocìation, N.Y., N.Y.

}¡I SCON -97 - February l9B3

Soap an Detergent Assoc'iation, 1981. llisconsin Lakes Study, 1981:Protocol. The Soap and Detergent Assocìation, N.Y,, N.Y., 30 pp,

Soap and Detergent Association, 1980, þl'iscons'in Lakes Study, 1980:Protocol. The Soap and Detergent Assoc'iatìon, l{.Y., N.Y.

Soap and Detergent Assocìation, 1979. l.lisconsin Lakes Study, 19792. Protocol. The Soap and Detengent Assocìatìon, N.Y., N.Y.

Soap and Detergent Association, 1.978. Hisconsin Lakes Study' 1978:Protocol. The Soap and Detergent Assoc'iatìon, N.Y., N.Y", 36 pp.

Souzognì, H. C., P. C. Uttormark, and G. F. Lee, 1976, A phosphonusresidence time model: theory and appì'ication.' l,later ResearchI 0:429-435.

Sutton, C.S,, and S. Lansen,1964. Pyrophosphate as a source of phosphorusfor pl ants. Soi I Sci . , 9!_2196-20I.

Stevens, R.J., and B.M. Stevlart, 1982. Concentration, fractionation and' charactenization of soluble or^ganìc phosphorus 'in river water enteringLough Neagh. hlater Research, 16:1507-1519.

Stumm, l,l., 1973. The acceleration of the hydrogeochemicaì cycling ofphosphorus. þJater Reseanch, 7: 131-144.

Taft, J.L., l.l.R. Taylor, and J.J. McCarthy, 1975, Uptake and release ofphosphorus by phytopìankton in the Chesapeake Bay estuary, U.S,A. Mar.Biol. 33:21-32.

Trautmann, N.14., C.E. McCul'loch, and R.J. 0glesby, 1982. Statisticaldetermination of data requìrements for assessment of lake restorationprograms. Can. J. Fish. Aquat. Sci. 39:607-610.

' United States Department of the Interisr (USUt), 1969. Provisional AìgaìAssay Procedure. Joint Ind. Govt. Task Force on tutrophication, USDI,Co rvaì 'l i s , Oregon , 62 pp.

U.S.D.A,, 1978. Soil Survey of Columb'ia County, !.lisconsin. U.S.D.A. SoilConservation Service, 286 pp.

Uttormark, P.0., ì975. Hisconsin lakes accord'ing to trophic index number,pp. 12-23. In: Classifications of Wisconsin Lakes by TrophicCond'ition, Aã-õ-erson, G. (ed. ), l^lisconsin Dept. of Natural Resources,Bureau of l,later Qua'lity, Madison, l,ll, 108 pp.

Uttormark, P.D. , J.D. Chap'in, and K.M. Green , L974. tstimat'ing NutrientLoading of Lakes from Non-Point Sources. Environmental ProtectionAgency Publ ication 660/3-74-0?0.

Vallentyne, J.R., L974. The Algal Bowl-Lakes and Man. 0ttowa, Misc.Spec'iaì Publ . 22, Dept. of the Envi ronment, 185 pp.

I.IISCON -98- February 'l983

Verry, E.S. and D.R. Timmons, 1982. Waterborne nutrient flow through anup1 and-peatl and watershed i n Mi nnesota. Ecol ogy, 63-: 1456-1467 .

Verhoff, F.H., and ilI.R. Heffner, !979. Rate of availability of totalphosphorus in river waters. Env. Sci. Tech., 13:844-849.

Vollenweider, R.4., I975. Input-output moclels. Scheweiz. 7. Hydrologie,37:53-84.

Vollenwejder, R.A. , 1968. Scientjfic Fundamental s of the Eutroph'icati0nof Lakes and Flowing þlaters, with Particular Reference to Phosphorusand llitrogen as Factors in tutrophication. 0ECD Techn'ical ReportDAS/CSI/68.27, 159 pp. Revìsed 1971.

hlDNR, 1982. Report on the Water Quality Related Effects of Restrictingthe Use of Phosphates in l-aundry Deterqents: January, 1982. l¡laterQuality tvaluation Sectjon, Madison.

I{DNR, I975. Classification of l^lisconsin Lakes b.y Trophic Condition: April15 , I975, Anderson, G. (ed. )o l^l'iscons'in Dept. of Natural Resources,Bureau of Water Quality, Maclison, I^lI , 108 pp.

Weaver, P.J., 1969. Phosphates ìn surface r¡¡aters and detergents. J. WaterPoll. Control Fed., 4It1647 -1653.

}letzel, R.G., 1975. Limnoiogy.

hlilliams, J.D.H., H. Shear, andScenedesmus_ quadri cauda ofseðî men ta ry ñãEFlãTlTrom25:1-11.

l,lillìams, J.D.H., J.K. Syers, S.S. Shukla, R.F. Harris, and D.E. Armstrong,1971. Leve'ls of inorgan'ic and total phosphorus 'in lake sedinrentsas related to other sedjment parameters. Env. Sc'i. and Tech., 5:1113-1120.

l^Ji sconsi n Geol og'ical and Natural Hi story Survey , 1959. Soi 1 Survey ofOneida County, l,Jisconsin. Wis. Geo. and Nat. Hjst. Sur., 59 pp.

t{isconsin Geologìcal and Natural H'istory Survey,Ig47. Soils of LangladeCounty, bl'isconsin. I,'fis. Geo. and Nat. Hist. Sur., 6'l pp.

l{isconsin Geological and Natural History Survey, 1927. Soils of l^lisconsin.hlis. Geo. and Nat. Hist. Sur., 270 pp.

l,lisconsin Geological and Natural History Survey, l916a. ReconnoissanceSoil Survey of North Part of North Central l^lisconsin. l^lis. Geo. andNat. Hist. Sur., 80 pp.

hlisconsin Geological and Natural H'istory Survey, 1916b. ReconnoissanceSo j I survey of l{orth Eastern l.l'isconsi n. l^l'is. Geo. and Nat. H'ist.Sur., 87 pp

W.N.R.B., 1977. Report to the llatural Resources Board of the Ad HocPrivate l^Iastewater Treatment Systems Committee: l,larch 1977.l^lisconsin Natural Resources Board, Madison, l,'fisconsin. 70 pp.

l^1.8. Saunders, Ph'il adel phia, 743 pp.

R.L. Thomas,1980. Availability tod'ifferent forms of phosphorus andthe great Lakes. Ljmnol. 0ceanogr.,

hliSCON .:99- February 1983

l{oo'lhiser, û. 4., B. A. Stewartr H, H. l.Jischr¡eier, J. H. Caro, and M. H.Treren 1975. Control of v+ater pol.Iution from cropland, Vol. I.EPM6At/?-75l026a, U. S. Environnental Protection Agency.

Young, T.C., J.V. DePinto, S.t. Fì int, l'{.S, Switzenbaum, and J.K. Edzr.rald,.l982. Alga'l avai.labììity of phosphorus'in nunicìpa1 waster+ater. J.t.later Pol'1. Control Fed., 54:ì435-1528.

Young, H.L, and S.Fl. Hindal l, 1972. blater Resources of l^lisconsin ChippewaR.iver Basin HydrologÍc Investigations AtJas HA-386, U.S.G.S., 4 pp.

ï,lI scO¡l -l 0r- February .l983

APPINDIX A

Maps of Study L.akes

Figure Al: BALSAM Lt',.c (Test)

LAKE lìrrl.¡nrst(:rt()N 2(;.3î. 1'1. 15

RA¡,i(,} I l) \\l<>vs lì¡rr lrrr,rorl'I ()u NsHIP { i \

l-qPc-GtaPHlc !,Y!vlB9-Ll

a¡vs' Èluaa ,- ------'----O!Áe, !v 14rú. t -5FÀ.ù!., e¡.'-, - - - - - - - - - - Òrr*o¡ sPÂç*F--- - - -- ---- _tÍao ¡tc-,-- ---------_CRoi¡ì 5dc¡:.- ------ - -"' - :"''

OrEL.'¡ú -- ---- --- - _--__l¡É¡r¡ôNrt a*arr no- - -- - - - --_ "ñ€sc¡r. - - -- - - --- --- i-- - - E

5r[ÉÞ s.3PE--------= = =

sÞÊ\a-- -.------- O'-ñfiRHr:'[!' rrltl--.

--*ÞkulF- - - ---. --- ------- --::j*o!o€D---,---- - --- ------ OÞÀs'uFto- - - - - - --- - - - - - - - -Øcu!ì¡valÉo-- - - - --- ---- -- -Of{Þcr4cH SFOitÞrÊsAltNl rñLEl- --- -':-PEF&teñr ouÌLÊf---

-ã¿J¿-*Âe5H___-_------.4

- 4

pÂF¡ÁLrY w*ofg---- --- ---@cr.aFlg -----,----------O88il(ts {ARX- - - -- -- --- - ---89

LAKE 8OTÎOM SYMBOLS

?[ir b rlrr øly \drogropli< æp ol t{rir lolr ovoiloþl¡.prod*od hon *igiñol .hoô ol Dêø ol Ñoturol lc'

A U. S Gælogicol Suaoy l{og ir ovoiloble lron u¡ ¡how'in¡ *,c ooo (oipror. l2 ¡quo¡c mil¿¡) odlo<lht io lh¡t lol''

To o¡dcr ¡æcitr H rt '- L3k'' ¡:;;;;:ã;:

t,

.\.**,.- -\

I

-JI

'ir ,/'<l)

till

lu/,

il1t

i!

'Èi!Ìræ t:_ f - i

!!\ . .r *l:;¡T=;i

é."3,à'eg

' Lil

\\\\=::__=\\\\\

1!;¡1::-.,* CLARKSON MAP724 ÞtSNÕYÉt SlrtIr

Kruk¡sn , Wìr¿*uin $¡¡190

WÀSHBURN COUNTYMopNo. ltltìl

co.*{-';;*;:1

FIGURE A2: Butternut Lake (Test)

__"51-lq#l*Mcp No !rr r

LAKE llullvrnut5¡ç¡¡¡¡p .1. 5. 8. 9- t?. t8-3:1, 33n^N(,r I uTou\ L!\(' (h¡r'r,('Ba1Os¡5¡¡¡p 40.1 1 li

tli h Í. slr blórry.oph ry ol rl¡¡ t¿. oFiiôU.,Pd6Gd loñ d€,€¡ clôñ .l br o, ku.d t.-s'<.r - M¡sA U 5 Goolryrcol Sr-r &Þ i dvô¡¡obl. h* a .¡.:.t! h 016 lopp'ô¡ l? F6r. ñn.rj ôdpc.nr þ rhd tol..

1ó qd.' ¡È'ry X. n¡¡cd\'

ì- - :_:-;___-.i_..

-::-l;: Ì -.- i

--- -- -,,_.-* -.- :----- -- .t-- --

.-+Ì .- - -l--

.+,.l ì --

IMAE tllq3 !úa aotro¡ ttrto!!Q r.-r nrf,¡¡ !Þ, rÞ ? h¡ h,...r!1 È,dh

---r..

s-r *.L ¿ ¡,tÐ. . ,¡ð9?'î *îJ,Þ¡t . .r., ¡ .*r * r.ia'¡-ç ct.r.. É Þr{ ¡. h,r , b.- -r...,,_

--_r.Þi-rrrd.r-. 9 5 I !-,,r.¡t,.a.r.r¡¡(ò; ¡.*rÈd : r.-.r .s l, rnr ¡ rr..,,.. rrP,.,,-¡_rF¡ h R h-.r d5 ¡r &d r ¡d

-brlFq ú b I i&¿ a^tr tÃt. 3r.rr d H ¡r r.rr¡;c-'

@IÞl\)I

*h(*qF'?F: li",r{lJrb. .-: xti'¡r, -.I

S;" 't'nir.h *_-

d, hr'&tÊq&¡i.r

n-&dr &Ei,srksr;n únyøyfrulm, tf¡aæh SfttorÞ taa.. - &cE ttñ hte - E LÉ,

tlaP No. 39?

!-al!E_-g-ar Ïg!!-lvl{ggtsPlLPY PEAI----.----PMUCX -- - - -- ------ -kciaY------------.csañt-------------sRUBEL!----------.R

iMEPGENT VÉ&I---.!FrÊÊoús PEAf__-__-_fc[rRrrus____-_--__DMARL _____ _ __-_--"MGñÁVEL -, - ------ --G8!DFOCi--_- _____-ArsEÞct vtcEl__ -T

FIGURE A3: ELK LAKE (Test)

Th.i 'r

rb ú!! (úr€r ftÉ cl rh,r or. 0'6 )ob¡. Þ.øuc.é r,ôÈ d,t dl ({tr ê¡ W,sst,ó Cmçryo"on }p' M!¡ !'i

A U 5 C*otoç ¡oi Su¡vcy MoF rs oçc¡lôbl? fronr ut ¡ho*rrgthe ôrêq ropp'or ii rquorr m,l.s oCJo(e¡r ic rhrt lote

rHrs rs ^ cløtkÁ0[f, rrx: suRvEy MAp oF u^.r-_--ÃLlf-

...'l*-- -. z:1¡--TowNs¡rP- JJ------"Ra{GE --.-L.--- ercwN or vfqC65TÉR-couNrt----i:lçç-

I

(,I

P!!1'\h.. ì^i iì tt¡ 51't1d l,

rllc C{nfrkÁ¡fi, mer co.KALIXA!*.4 WISCC\SìN

Púii,rr,. ¡, ! " .. t.,,:, ..! Mô., ,, ..!\a.W'r.-".. -..rrn!rn. fF¡.."-..i

FIGURE A4: Enterprise Lake (Test)

LAKTSECTTON '1. l. ll l(ln uCr l0 l-ì

Tos'N ti tr lr'r

TOs'NsHtp :Jl N

lo¡a-q ? a? lil ç* 9Yit99 Ls

Þ.9sP {ruq. -.-, --------_osÂÞ. ¡L i3ñ!. I -gtÁtM\f 9¡ ¡ -------- --_ - - -$'rnO* SP¡*!a'--- - --_- -- -tr¿r" å¿o- --- --- - ------ -g¡Oc/t 1ÈOAL- ---- - -' -- ' -' 'l::tOrllL rG---------_'' - -'--'aa¿nfcr¿c cwE!!¡rG- - -- - -- ---EFE5oF!- -- --- ---- -- - - -- - -Es1:åÊ s-oPt-,------

= = =sPÉ,N6-----------¡triaRp'-tñ' iN.El--, _.--8Ê!5h-- - --- --- - -- ----- --':lrc,o¡Eo-- - --- - - - ---- - - - -- €'PASrui€D- - - - - -- - - - - - - - - -c9au.r,vArf o-- -- - -- - - - - - - - -AÊrttúÂ!ts sFoFE

PtRMAtofN'ltlEr---- -<ÞqRMÂ\Eryto!T!gf---- >

-MACSÉ-___-------.4

- À

Þapr,aiLr wñ¡Êo-- --- -- ---l.OcLEAR€o- -- - -- - -- - --- --- -OSENi¡ vAR'! -- - ---- -- - ---.B'}

LAKE Eqf--IoMlYflrgt9PUsÞf P¿Àf--------.puN.-r--------. ----,CLÂY-------------asÁNc------------.9

Ê.€MÊR6ÉNf v.c1---.¡FIBÊOUS FEÁY-.--.-.FDEtR'uS-----'--- - iu¡Fi__-----------I6RAvEL-----------6

56{Fq{ V€6Er---r

thir h rh. oôlv hvd.æ'oçhk rcp ol rh'r lolc ovoiloblo'

p.lir..¿ f'.,i -çinãr cr'ot of O'Pr ol Norvror l''þurc.r - l{od¡sA U.5 Gælogicol Ssñ!' ,åoP i¡ ovoiìobl. l¡on ur rho*'ing rìrc oræ (oppror l2 rquorc milc¡) odlotrnt to lhb lolc

To ordcr rrc¡fy I nr'-'¡'r), tsc & Ll( hål;;;ã¡¡

LÄNGLADE COUNTY

MAF NO. I 08?

III?t.,

¡I

\

II

@

rit.I

| .q __; . ¡r: 1É .F..- ¡:oi L,!1aF.E 1r¡r¡I ..-- 'ú¡'¡^. ' hd L!'''

I

l

Tï

rtI

r

I

JI

t

ÞI

- -* r1¡,

Þ \I

o\

lti.!if

:r!!:'.1-:1-

r.rt...t. s! f4¡l¡d.ltt ¡t tdt¡ Ftr r a

r¡¡ dr'¡___-_-¿J.lrrlt¡( ^!¡

h tt¡vo!e¡t-.-&'(rl tr¡^rr !6!.¡r---lLrtIt!À¡9 3da.r{..gtr

CLARKSON MAP CO.7?¡ te5{OYIR STrEEÍ

Kluk:unr, Wi¡<onrin 5¡[]30

FIGURE A5: LITTLE gEARSKIN LAKE (Reference)

ONEID¡, COUNTY

Mcp No. 4762

LAKE I-l1t le [ìe¡rrsk¡ng¡ça¡6¡ I l. 12

n¡¡'¡cr--lË-1'61¡'¡ ('as¡:an

a91¡ ¡5¡1¡p.3 ? N

fhir ir thr onl¡ hydrogr6phr¡ nop ol th,r lol¿ o,o,iol¡|,

i:l:,.î1t* o'çinor (hoô or D.p, or No,ú'or P,

A U S Gcolog'<ol Su*çy ¡4oO ß ovoiloblc f,o¡ ur ¡fo,¡ng rhc orco (opp,o¡ ìl quotc hilr¡) odto(cñr ro lh'r l.l

'to o¡dc, ¡pcc,lr Hcifft'rcl J,¡!tJ#..T--.-

. //t¡ltrtl ^^11^^^^ I- n' btjllldl$CIifl út¡,l¿zt(¡ul¡unr. \{iror¡in 54130

e au

I!¡(nI

ç/ I

.1/¡it

of

I

T 0r0 0i A¡h rc

Q r',"lry r.rrr.rtr ñÍÇ tooo.o

f, rn"-.0@ e¡,,<.,,r'rt

E rr.o'rfD c..,

gYiËotsrlll¡tl' g Itt, rlarr_--- hart,.ila ¡ñarat¡tálìl,"'."_-- I¡t.rÞin.nt

!0ff09 !Y9!0!3t to!larrl& 5ùñr¡ I Sol.tq lc.¡ ¡¡ns 1. siftltt $ü0.ñt r.t.lo,i{¡ f¡.rt.ñr rta.'0t'ú

^ fl..llâ¡ rrtrt!t¡..

+ ir!.¡ iirllart

*^raa o"ao ,aa, ^a"aa

uxoEa 5 F1. 17 fovË R 2â Fl -_l_ a

I¡r of,PTH 27 rÉ€l'10r^L ÂL(.____19_PP.Xv0!u¡€._-g!l_acRÊ Ff.s xc RE L ri[ _-_l-9__ l.( L € s3. x,¡.¡ of Sôorar,ñ. f¡c¡!é,hQr¡þ.ô

!¡r¡

c. crlt

.7t#*ffi: P.,-o^.rr 6l.t

={ t.rñôn..1 .¡tl.t

rJv oc.O.r-i.9t.r..-d bd

31 5;Û O Acattr O Accita Yltì P6?llô9 - Bool Llrart

FIÊTIRE ÅS¡ M0çS LAKÊ {Test)

tu'lvcrt ta Lnnrg Lake

--.46-

FIGURE A7: SWAN uAKE (Test)

LÂKf Suans[c]to¡'. 5. ti. l!1. l. ?.8- 11

R^N('r --9!'o

t'1¡1q¡ r ['¿e lf r'

r rtu rrttlP l2 N

o.\ !

llir ir lh¡ onlv hvdrærophk 6p el rhir lolr o'oilobl¡'p,o¿rod lroi "r,gi""t

.toa ol Dcpt ot Ñorurol Rç'

Þv.c.r - ,'{odiþrA U S Gcologicol Svney Mop ¡¡ ovoilobl¿ lrm u¡ rhow'

i.g *. "r". f.;"-t ì? rquori øilo) od¡o<'nr lo lhÍ ¡olt

To o,d.t ¡Pccib Porl'age 6- - ----

COLUMBI.A COUNTY

Mop No. 1489

,lt' rgnt kson

..,1^.

WAfER AR¿A 405 88 ACRES

UNOER 3 FT. lo

ovER ?0¡L 63 %

I'AX. OEPTH 8? TEET'

TOIAL ÂLK. 2IO PP.M

voLuME 12.8975'6 ÀcRE Ff'

S HORE LINE 6.04 MIL ES

c'rÅ

/,sO'

[rukrunr, Wixon¡in !l4l3O

,o,o.o"ô '7J.

t-/

lt

t5o'iæ\

(t''i{¡

,14=i././- j' /I

\¡I

,'l/:,'//,

IL

þi\-v,. $lt !

4""ci,ìo

/ (.ô-i'"<íi*<''

top06i^PHrc sruEoLS

Q Arurl ¡rlllll. 5ttl9 ¡lotl}ti. Þorl¡o¡lr @dad -- \- lñ6.r'ñ'la tño.al¡{Þ) wooa.¿ á4jÈ Yo""fi crro,cc

-¡--" 5e'';9

@)rorlurcd ---.lñt.ri¡ll.âltl{oôO ^çrtrclru?.1 =:=¿

Þ.rnoôrñt rôltl

ß.t g.¡(à ilo.l =

P.'ûoñcñl octl¡rr c,?rrin9 rJ: Don

ÁB

/ -\è-l^i,! t'" ,,/

LAXE EOTlOM

P P.oI B

f¡ Mu.l ¿c. croy .i.x. Morl 'f

5d.5oád t9! s¡lt ¡6r Groral ðR. F úÞþ1.

Er 8?oro(l

SYveoLSgould.rigt !ñtr â 3ñoCt

Rocl óôhg.t lo ôôr'golrat

5!ùñ.'g!nl r.q.lotioô¡ñar9.nl v.q?lltioñFloôliñg rlgaloiioñ8rùth tòal¡ar¡

/1 ^rõ,J'. q},

E nr¡o,tÉ co¡¡

LL_LEo3-¡;--Åi< g É6ii I'4n'_gæ --\ \'rÈr ' \

"o\"1)

'--+"\ trf-*--

rox R,iii

O Acca¡¡ o Ácct3' rllh Portlñg ' 600l Llv'?t

O.t.R. Srot. crúá loid

FIGURE A8: TEAL LAK¡ (Reference)

fhir ir rhr øl¡ lyrlrogrophi< aop ol rhir lolr ovoilob!¡.¡odutod fron orieínol rhon oi Dcpt. of Nde?ol tc-þu.a.r - lodisA U 5 Gooloe,<ol SsÈ.t Môp ir ovoiloblc l¡oø v¡ ¡hoç.iag tho oræ (oppror l2 rquore mi'c¡l odto..nt to th¡r lo!e.

to ordcr rpccify \anrtkaEl¡,n l,¡Lhr:.---,-

M,r.ó Hord¡cod å P'ña

usa

u¡¡oER 5 FT._-____!_ Í

l¡ 8q!!

'loraL ÂLx.___lQ_e P.Í.voL ux E_Jãlgll__^c RE F L

_-j]L+ sHoRt L|NE rt 8 xrLES

s

5raa, !toptiñdattñ¡ta ¡ÀO,atlæ

Sfl,õit.tr.ñ,ttanl ¡traOñ

Pa îo^tât o!ttai¿¡ô ñS!¿r..rô.ó tond

!orr0H SYaSoLs

B 8úuld..¡t St!ñpr t S¡9r

'11: locl !.^r. i¡ ñor,gÉ1r..t 3uòR.!..' 'rt.to1's¡ f6.,9r.' rrtrtêr¡o^Â floô!'¡g '.0rtal,o.+ 8r!l¡ tr.'r.'l

LAKE5¡6a¡9¡ 26.21.28.33.'li{n¡-vCr 6 \l'Tcr$'x So:çlc r Lakea6¡¡'¡¡5g¡P 42 ¡-

CHEOUÀMEGON I

NATIONALFORE S'T

SAWYER COUNTY

MopNo. rÌ5?

.X

"4"JíC):!-Y'

@I

æI

lrloñd(sror. orñcóÌ

.t't á

È.

:I _---l

roP06q¡PXlc sYHBoL

Q e,..t ,¡¡rt¡Þt Þart,olrt ¡6ó.d -z\-@ rooc.o :;*.ç!c

, cr.or.ó(f.'Forturra

@. r9,'rvrrurot æ<Lv g.^cf lorr

-1¡ Orrll¡ñg r-!:B Prto'r O.r.R.E) c¿.p

88 MILE9 OF SHORELINEÊXCLUDING ISLÀNDS

<, Âcc?!r rlth Portlng - Bool Lliitt

U,¡çO noróroo! å F,ñ.

!¡it

C Clot

9ó Soñó

sr 5.rt6t 6'orarr ß eÞèra

tr 8r¿ro(l

ñ'3RT

leo/ Ptñ tlcrcg€71 7 Ac¡¿s

9'

O ^cctr¡

?0 Mriʡ ro Hoyrord

LÄKE 'f osnlinesrcTtoñ- 6. :ì ì

R^NCÍ 11 Iit O\X'N 'l'iìr'(e Lakc:s'r'Ov N\HIP 38 ' Jf' \

lhir ¡r rh. alb hydrw¡ophic ñoP ol tii. loh ovolloblc'

pro¿,..j r'"'í o'r,glnãt cun ol Þcpt cf r''¡oterol ßê'

A U. S Gso¡cEicol Suaoy l{op i¡ ovoiloblc l¡on o ¡hos'

,.n]*" "'-,.'pp-t l2 quo¡c ¡;lo¡j odio<ant¡o rhi¡ lolc'

1o o.dc,.pc<¡ry Th'ee Lakes 6l ;;;¡:

¡r;,¡¡.

FIGURE A9:

o.

\e\\\. fi\\-

\\

ll

r¡it torfot 3Y*!oLst. l.rl ¡ l.,rlt'¡Ir ¡u!¡ ... St!.t¡ I 3.at.4 Cr¡r ii ¡oct o¡ry' r...ft¡¡¡ t.rr t !¡!bÑrl.nr ia!.tcilt!a. !0.ó ¡ t'.'r..r t.a.'rr't3r tllr ¡ fl..tl¡9..t.r.|¡t'St O¡c.at ì Itv.r ¡Þritr

l( !.d.*¡

TOI^INLINE LAKE (Test)

ONEIDÃ COUI

Mop No. 47i

@

&Êfisvksom C,,rr/,yK¡vk¡un¡, Wixon¡ln 5¡1130

:l

I¡/l:'

,'r

o

ù

IÞ(0I \

P/t'

lit

\\.tì,oll

.rål i

I

@-r'i ì --=.l r

fofocttñlc SrxlolaQ ¡-t" ,iltil¡ sr.., tl.r.i¡¿ r¡'r'r!¡ ilr.a --_.- ¡ñ.?rrnii. rt.r.lir

Q r*o.o áÀ, ¡t r.r'¡k Crr.r.a É Itr'ôl@, ror-.r ---

¡ñr.'irr.'r "{"

6) ^0"(e'lrfo¡

¡==- P..ñ6ñ.õr ¡ñlrl

; ¡.ñ(È ¡ôil Êæ: P..òoilñr !¡tltl. D,.r¡,¡l JY Oo¡lE ¡.¡¡'r o.l.i. Stolr .rùa bóaIII c¡¡r

E¡¡:É-s'-+'Ei '.it¿ ;I i"i¡ :r

r.le 4

i! Þ!!! ir_l

ii-r í;r,r-l--Ilj'&"^;;.i- -r-¡l-'4ù:-::itr

rÀf E ñ ÂRÉÂ-åiÂ---¡cRtsuxoÊÞ 3 Ff ------i-- aovEÊ eo FÌ--j- 'É

ì.ax. OÊPTts_ rq J€EL'tollL ÂLX,__I5-P Þ ll.vor u{E_-___19-ÞI_ac ÂE Fl.

S HoRÉ L r NE ---¿J-- xr L f S

'\Þ.=\/,''-"\---__.--_r'

/ ,*-\. \----. .!,:.,;/,

ì\--o------:*.tyÆ

..o

O ^crrr.

+ Açqct. rllt Po.llôl t âcot Llv.rt

APPENDIX B

Description of the Multívariate/Muìt'iple comparison Analysìs

APPENDIX B

Desc ri pt'i on_of _the Mul t i va ri ate/l"lul ti pl e _Compa ri son Ana lys i s

The Statìsticai Model

The three response variables, tota'l phosphorus, chlorophylì a and

Secchi disc depth, were analyzed separateìy. Measurements of a variable

for a lake in a year were analyzed as a vector response. To make the

responses commensurate across years, meâsurements 1 through 7 for 1978,

1981 and 1982, and measurements 1 thr"ough 6.and B for 1980, were used. The

responses are thus seven-dimensional. All responses were transformed by

taking base 10 logarithms. Fish Lake was omitted, as 1982 data were not

collected, so nine lakes were used.

The data on each response varjable were analyzed as a multivariate

two-ttay layout. Two analyses vtere penformed for each response: one using

only data from site 1, the other using the average of the (ìogged) data

from Sites 1 and 2.

The model can be written mathematicaìly as

xijk=uk*Yit *Ljt*.íjk

(i = lr 2r3, 4, j = 1, 2, 3, 4, 5, 6, 7r 8r9, k = 1, Zr3, 4, b, 6, 7),

where Xijf is the kth observation on lake j in year i, u¡ is the kth

component of the grand mean, Y.¡L is the kth co,nponent of the effect of year

i, and L¡k is the kth corponent of the effect of lake j. The enrors

i*.ijl, eij2, .i¡3, "i¡4, .i¡5, .ì¡6, ..,rr)TÌ are assumed independent

seven-variable Gaussian w'ith zero mean and covariance matrix x. The advan-

I.II SAPP -81- February l9B3

tages of this model are:

1, It takes account of the covariance structune of the data,

2. It is simp'le, allow'ing for differences between lakes and yeans

without assuming a specific mathemat'ical model for the

di fferences.

3. If the simpìe analysis of variance model is unable to detect any

effect due to the ban, mone compìicated models would not be

worthwhil e.

Parameter Estimat'ion

The multivariate analysis of variance cìosely parallels its univariate

countenpart. Maximum l'ikel i hood est'i¡nates of the ef f ects are gi ven by

uk = T..kt

v -'f -ìFtik - ^i.k - n..k'

Ljk = T. j* - T..k,

where the dot and ban denote averaging over subscripts. The maximum like-

lihood estimate, i, of the error covariance matrix, is pnoportional to the

error sum of squares and cross products matrix E, where

49 AA

Ekl = il, ¡1, (xiik - rrk Y'o - L¡¡) (niit - u1 - Yit - tir)'

Estimates of these gìve one an appreciat'ion for the correlation structure

I.II SAPP -82- February 1983

as well as the variabil'ity reduction for the ana'lysis based upon the com-

bined Site I and Site 2 data.

Hypothesis Testing

The statistical tests of interest are multip'le comparisons of

contrasts Cik = Yik. Yr*, denoting the difference in measurement k between

post-ban year ì (1980, 1981, or 1982) and the pre ban year, 1979. The

ci* are est'imated ny ôir = iir - irl (i = 2,3,4, k = 1,2,3,4,5, 6,

7). He shal I fol I ow the devel opment of D.F. I,lorri son (1976).

By formula (8), pp.200-201 of Morríson, the 100 (1--) percent

simultaneous confidence intervals on the {Cif} for all n'ine lakes are:

ô,0 - ,i"¡,¡l r/2 <cik * ô,* *,+r,\r,t".Here Xo is the upper 100* percentage point of the greatest characteristic

root di stribution w'ith pararneters (in Mor.rison's notation) s = 3, n = 3/?

and n = B. l.le take * = 0.05, and find from chart 11, p. 381 of Mornison

that x- = 0.625. simi'lar expressìons can be.displayed for the other

situations discussed in the Methods Section (Multivariate Analys'is/tfultiple

Compari sons).

I{I SAPP -83- February l9B3

APPENDIX C

Description of the Approach Used to Develop Phosphorus

Nutri ent Load'i ngs

APPENDIX C

Descriptiojt of the Approach Used to_ Develop PhosphorugJutr'!-ent Budgets

Phosphorus loadjngs to a lake can be segmented'into tributary input,

dirêct drainage and atmospheric input" The tributary input would resu'lt

from any runoff from areas which eventuaììy terminate ìnto a stream

draining into a lake. þlastewater'därived 'input wou'ld account for both

sewered areas which have d'ischarge po'ints into the lake direct'ly, or a tri-butary to the lake, as well as septic tank/tile fÍeìd system seepage or system

failure. Direct draìnËrge would arise from areas direct'ly adjoining the

lake shoreline, areas which do not dnain to a lake tributany, but rather

drain to the lake itself. For atmospheric loadings, onìy the wetfall and

dryfa'll which enter the lake surface area directly are included in this

categony. Thus, the total of these inputs would comprise an estimate of

the combined phosphorus loads to a lake from various sources.

The areas drained by streams and lakes, and land use areas, were deli-neated by surface morphoìogy as provided in.the most recentìy updated

U.S.G.S. topognaphic maps.

Stream fiows wene determined utiliz'ing data presented in the hydro-

logíc budget sections of the U.S.G.S.-University of þ{isconsin Geological

and Natural History Survey hydrologic atlases (01cott, 1968; young and

Hindalì, 197?; and Oakes and cotter, 1975), suppìemented by norma'lized

stream flows calculated by the U.S.G.S for the National Eutrophication

Survey (NtS) and National 0ceanic and Atmospheric Administration (N0AA)

monthìy preci pitati on reports fon l.li sconsin.

The procedure for determining runoff quantities and flows involved

I.II SAPP -c1- February 1983

calculating a runoff to precipítatìon ratio for each year. The value

th'is ratio for an average year's precipitation was obtained from the

U.S.G.S,-Un'ivers'ity of l^lisconsin Geological and liatural History Survey

hydroìog'ic atìases or from streamflows provided by the U.S.G.S. to the

To ôonrect for the dìfference between the precipitation of a test year

that of an average year, an assumption was made that the propontion of

runoff to pnecipitation could be moàeled by the average basin data for

average, and wet years in the Upper Hjsconsin River Bas'in (Enterpnise

Townl ine Lakes) and the Ch'ippevra River Basi n (Baì sam, Butternut, Elk,

Moss Lakes). For Swan Lake, located jn the.Fox-Wolf River Basin, the

va.lues for the Royaìton-New London anea were used since average basin

val ues were not avai'labl e.

of

NES.

and

dry,

and

and

'--*---/

To clarÌfy the procedure, an examp'le calculation of runoff (cm/yr) and

?runoff rate (m"/yr) us'ing data for Enterprise Lake is provided below:

l. The average year precipitation and runoff values for the lake

were estimated from the U.S.G.S. atlas maps (Oakes and Cotter,

ì975) which show ìines of equal precipitation and runoff for the

Upper !f i sconsi n Ri ver Basi n 'in whi ch Enterpri se Lake i s I ocated:

Lake average year precipitati on = 72.6 cm/yr

Lake average year runoff = 30.5 cm/yr

Lake average year runoff to precipitation natio = 0.42

2. The general relationship between runoff and precipitation in the

Uppen l.lisconsin River Basin was characterized using mean basin

data for precipitation and runoff during dry, average, and wet

years provided in the U.S.G.S. atìas:

I.¡ISAPP -c7.- February ì983

Mean Basin

Precipitation

(cm/.yr)

60,2

79.5

10t.8

_{crnf .L_

Mean Basin

Runoff

1 7.0

3l .5

46.2

. Runoff to

Preci pi tati on

Ratio

0.28

0.40

0,45

Dry Year

Average Year

Het Year

Through interpo'lation, 'a facton vras obtai ned f rom this tabìe,

which, when added to the mean basin average-year runoff to preci-

pitation ratio, provìded an estimate of the runoff to precipita-

tion ratio for the actual pnec'ipitat'ion whicli occurred during a

study year. The first and second terms of equatìon (a) represent

the difference between the runoff to precipìtation ratio for a

dry and average year at tnterprise Lake. The lake average year

precipitation in equation (a) is the avenage from the NOAA

weather stat'ions, not the U.S.G.S. atlases. These terms were

then added to the third term (lake average-year runoff to preci-

pitation ratio) to estimate the ratio for a study year at

Enterpnise Lake.

}lI SAPP -c3- February l9B3

r-1I rux. rake I

I uug. year - study year IDry I pfeci p. _ preci p. I(a) Year = l lxFactor I Orecìp. for - precip. for I

I avg. year dry year' IL]

]

mean basi n

runoff topreci p, ratiofor dry year

mean basinrunoff toprecip. ratiofor avg. year

1 ake runoff topreci p. ratiofor avg. year

The equation for the wet year factor was'obta'ined by replacìng

"wet" for "dry" in equation (a). If NtS values for the average-

year runoff añd precipìtation were avai'labìe, and the resulting

nunoff to precipitat'ion ratio was less than that fro¡n Step 1, thg

NES ratio was used as the third term in equation (a) (i.e., the

mone conservative runoff estimate was calcu'lated); NES values

were not available for Enterprise Lake.

Hhen the data for Enterprise Lake were used in equation (a)

the foììowing equations resulted:

(b) Dry Year Factor = (-6.eexlO-3) + 0.42

(c) Average Year Factor = 0.42

l- rake II zo.s - study y.u. I

L ?:;;;l; j

H I SAPP -c4- February ì983

(d) Wet Yean Factor = (2.Zqxl o-3)l- rake 1I zo.r - study.year

I

L ?ifiiJri l+ 0.42

Substitution of the precipitat'ion (cm/yr) at the lake during a

study year into equations. (b) or (d) provided the factor for that

yea r.

4. Multiplication of the facton derjved in Step 3 by the pnecip'ita-

tion (cm/yr) at the lake during the year for which the facton was

calculated provided the runoff (cm/yr) for that year.

5. Runoff rates 1m3/fn) were calculated from the runoff (m/yr) yalue

calculated in Step 4 and dràìnage areas (*2).

Lake tnibutary phosphorus loadings were estimated using flows and the

mean yearly phosphorus concentrations of the tributaries. For stneams

recei vi ng muni c'i pal wastewater tneatment p'lant ef f I uents, the ì oad'i ngs

attributed to the streams were detenm'ined by subtracting the treatment

plant loading from the total measured stream load, For several tribu-

tanies, insufficient l97B data, or no data at all, were available to calcu-

late loadings. Table C1 presents the methodologies for estimating

phosphorus loads from the unsampled tributaries.

Loadings to treatment pìants wene assumed to be 1.36 kg P/yn (3.0

ìbs P/cap/yr) for untreated wastewater containing detergent phosphorus and

0.96 kg P/cap/yr (2.1 lbs p/cap/yr) for untreated wastewater without detergentphosphor'us (SDA, unpub'li shed data). Phosphorus removal s due to treatment

bl I SAPP -c5- February l9B3

Tab le Cl :

La ke

lnlet concentration estimates used in constructing the nut.rient budgets for 1978. (a)

St ream ( m9 P/L) Source of Concentrat ¡on

Ba I sam

Butte rnut Spiller Greek

Schnur Lake lnlet

Mud Lake lnlet

lnlet from Birch Lake

Mud Lâke ln¡et

Butternut creek

lnlet from Lake Duroy

West lnletFox River lnletTovnl ine Creek

Maple Lake lnlet (b)

0. 064

0"083

o. 061

0. 051

0.062

o.o72

0. 055

o.o57

0. 104

a.166

0. 070

Measured in let concentrat ion.

The Mud Lake lnlet \r'as not sampled ín 1978,therefore the ratio of the Mud Lake lnletconcentratíon to the Birch Lake lnlet con-centration in 198l vas multipl íed by the 1978Birch Lake lnlet value to obtain this value.

Spiller Creek \r'as not sampled in 1978, there-fore tlre rat io of the mean of the 1981 and1982 Sp¡ I ler creek concentrations to the meanof the 198"1 and 1982 Butternut Creek concen-trations was multipl ied by the 1978 ButternutCreek concentrat ion to obta i n th i s va I ue.

The Schr¡ur Lãke lnlet \rr'ås not sampled in 1978,thereforc the ratio of the 1981 Schnur Lâkelnlet concentrat¡on to the 198'l Butternut Creekconcentration was multípl ied by the 1978 Butter-nut Creek concentration to obta in this va lue.

The Mud Lake lnlet vas not sampled in 1978,therefore the ratio of the 198l Mud Lake lnletconcentration t,o the 1981 Butternut Creek con-centration was multipl ied by the 1978 ButternutCreek concentration to obtain th¡s vâlue.

Measured 1978 Butternut Creek concentrations.

Mean of 1981 and 1982 i n let dat,a.

Mean of marsh-swamp values (Table C4).

Measured 1978 Fox River lnlet concentrat¡ons.

Measured 1978 Town I ine Creek eoncentrat ¡ons.

Mean of the 1981 and 1982 measuredconcentrat¡ons.

Etk

Enterprise

Sva n

Tovn I i ne

(a):

(b):

These values representand therefore i nc I udeSamp I es \r'e re co I lected

the tota I load ing of phosphorus ín the tr¡butariesthe loading from WWTP, lrhen present.only ¡n 198'l and 1982.

-c6-

were considered to be 10,20 and 90 percent for primary, secondary, and chem'ical

phosphorus removal treatments, respectively, and 100 percent for the Bjrchwood

(Baìsanr Lake) seepage ce'l1 and the Lac du Flambeau (Moss Lake) 'ìagoon.

No d'irect field measurements were made of septic tank/tile field loadings,

therefore several assumpt'ions were made. The results of the 1982 shoreline survey

(SDn¡ were used to estimate the"number of septìc tank/tile fje'ld systems 'in use.

The survey results are presented'in the lake descript'ion section. All lakeshore

dwellings (homes and cabins), resorts, and camps were assumed to have septic tanks

(undoubtedly an overestimation). Resorts and camps were cons'idered to be the

equivalent of 10 and 20 dwellings, respect'ive'ly, and to have seasonal occupancy

only. Other dwellings were estimated to be 50 percent seasona'l and 50 percent

year-round resjclences. A year-round occupancy of 2.5 persons was assumed for each

dwelling or dwelling equ'ivalent; seasonal occupancy was considered to be four

months per year. The per capita phosphorus load to septic tanks was assumed to

be the same as for municipai treatment p'lants. (The value of 1.36 kg P/cap/yr is

probabiy h'igh for seasonal resjdences which may not have ìaundry facilities or

other modern app'liances). A phosphorus removal of 90 percent before the djscharge

entered a lake was used for non-fai'ling septic tanks, whereas faììing septÍc

systems were cons jdered to have no phosphorus removal capab'i1ìty. A sept'ic tank

failure rate of 10 percent was used.

For atmospherìc phosphorus loadings (Uottr wetfall and dryfa'l'l ), the value of

0.175 kg P/ha/yr reported in the NES studies was used since it appeared to be a

conservative value. More recent studies (Reckhow et al., L9B0) conclude that the

NES value probably underestimated the .actual load'ings. The weather stations used

to estimate precip'itation at each lake are presented in Table C2; weather stations

were chosen on the basis of precip'itation data provided in the U.S.G.S.

University of l,{isconsin Geological and Natural History Surveys (01cott, 1968;

Young and Hindall,1972; and Oakes and Cotter, 1975), and the average (year)

precip'itation data in NOAA climatological reports.

-c7 -

Table C2z

Lake Weather Station

Average YearlyPrecipitation

(cm/yr)

National OceanoqraphicAdmini stration weatherestintate precipitation

and Atmosphericstati.ons used toat the study lakes.

Balsam

Butternut

Elk

Enterpri se

Moss

Swan

Tor¿nline

Couderay 7 W

Rice LakeSpooner ExperimentalFarm

Park FallsPark FallsPrentice 1 N andPrentice 2

Rhinelander

Minocqua Dam.Rest Lake

Portage

Rl.inelander

¡:ot avaÍlablenot available

73.4 (a)

83 .7

83.7

86. 6

76 -3

78.685. I?8. O

76.3

(a), l{hen referred to in the text, a value of74.9 cmlyt v,ras used for the averageprecipitation at Bal-sam Lake, based. on theU.S.c.S. hydroloqic budget (young andHindall, 1972).

-c8-

Direct dra'inage (the area surrounding a'lake vrhich contributes runoff

d'irectly to the lake rather than a tributary) loadjngs were calculated us'ing

export coefficìents compiled by Reckhow et al. (tgSO) ancl the respective.

coeffjcients applied to specìfjc land use areas. The choìce of coefficients was

based on precip'itat'ion and runoff quantities, the areal extent of individual land

use types, soil and geoìog'ical data from the U.S.G.S.-University of l,ljsconsìn

Geo'log'ica1 and Natura j H'istory Survey atlases (0lcott, 1968; Young and Hinda'll ,

1972; and 0akes and Cotter, 1975), soii survey reþorts (l,l'isconsin Geologìca1 and

Natural Hìstory Survey, 1916,â,b, 1927,1947 and 1959; and U.S.D.A., 1978), types

of vegetation, and fjeld observatjons. The. export coefficients were generalìy

chosen from the lower end of the concentration range presented in the ljterature

whenever data from more than one study were available, thereby y'ielding

conservativeiy low estimates for direct runoff (faU]e C3).

Severai deviations from the general procedure were required to account for

special circumstances. For Swan Lake, an export concentnatisn 0.057 mg PIL was

used for the direct runoff. This was necessitated due to difficulties encCIuntered

ìn interpretìng the effects of agricu'ltural.drainage ìnto the marshes on the

northern shore of the lake, the lack of information on agricultural ferti'lization,

and the relative'ly great distance (five km) of parts of the djrect drainage bas'in

from the lake. The value represents the mean of concentrations from trjbutaries

draining marsh and swamp areas (surrounded by forested lands) investìgated during

this study (Table C4).

At Enterprise Lake, the major potent'ial sources of phosphorus were marsh and

swamp dra'inage from the West Inlet, direct drainage'loadings, and septic tanks.

Since this was a test lake where runoff from the direct drainage area could be a

major source of phosphorus, great care was taken'in order not to overestimate its

effect. The location of marshes and swamps, and the topography, suggested

-c9-

Tabre c3: Export coefficients {kq P/ha/yr) used to carcuratethe J"978 direct drainage phosphorus loadings tothe test Iakes. Atl footnoted values are fromdata presented in Reckhow et al. (1980).

Lake AgricultureMarsh

& Swamp Forest

Urban andShorelineResidenti al

BaIsam 0.250 ( c )

Butternut 0.250(c)

EIK 0.250 ( c )

Enterprise 0. O

Moss

Swan

Townline

0. 1s7 ( d)

See text,based onrunoff.

0.1s7(d)

See text,based onrunoff.

o.1s7(d)

0.10O(b) Shore:

O.047(a) Shore:

0.1e(f)

o.r.e(f)

o.o o.o47(a)

A value of 0.057 mq P/L of runoffthe entire area (see text).0.250(c) o.1s7(d) o.oa7(a)

0.047 ( a) Shore: 0. 19 ( f)Urban: 1.1(e)

O.0a7(a) Shorer O.19(f)See text.

Shore: O.19( f)Urban: 1.1(e)

was used for

Shore: 0.19(f)

(a) Dillon, P. J. and W. B. Kirchner, 1975. For sandy soilsover granitic and igneous bedrock.

(b) DiIlon, P. J. and W. B. Kirchner, !g7S; Schinder, D. W.and J. E. Nighswander, I97O; and Singer, M. J. andR. H. Rust, 1975. For silt, sarrdy, and clay loam soils;loam soils over sedimentary bedrock.

(c) Harms, L. L., J. N. Dornbush, and J. R. Anderson , !974¡and Schuman, G. E., R. G. Spomer, and R. F. piest, 1973.For grazed and pastured agri_cultural lands.

(d) Verry, E. S., 1982. For forest composed of 70 % aspen,30 % black spruce and alder

(e) Kluesner, J. W. and G. F. Lee, lg74; and Landon, R. J.,7977. For urban watersheds.

(f ) Landon, R.J. , 1977. For low density resid.ential sub-division with large rots covered $/ith grass and. trees.

-c1 0-

Table C4: Mean yearly total phosphorus concen-trations for inlets with considerablemarsh and swamp drainage, and whichdo not receive discharges from aWãÈtewater treatment plant.

Lvnçh Creek ( Tea_l Lake )19BL: 0.068 mq/L (a)1982: O.A37 mg/L (a)

9fest Inlg! (Enterprjlse l,ake)1981:. 0.132 $q/L (b)l9B2: O.061 ms/L (a)

Mud Lake Inl,et (Butternut Lake)1981: 0.062 ms/L (a)1982: rrot sampled.

(a), The mean (0.057 mg P1L) of. thesevalues was used to estimate sometributary loadings in the L97Bphosphorus budgets (see Table C1).

(b) t Ont!¡ flve samples \{ere collected.

-c1l-

that some of the marsh-swamp areas (e.g., l-ijlson Lake) act as phosphorus sinks for

a considerable portion of the forested reg'ion around the lake. Therefore,

marsh-swamp areas wjth direct contact with the lake shore (either borderìng itor havÍng an jntermjttent tributary) were considered to contribute 0.057 mg P/L of

runoff (as discussed for Swan Lake), and r{ere assumed to receive drainage from the

forested lands (1.9 kmz) surrounding thern, whereas aì1 other ¡narshes and swamps

were assumed to be phosphorus sinks wh'ich drained 50 percent of the rema'in'ing

forested lands (2.9 kmz); the other 50 percent of these forests (2.9 kn?) were

treatecl as contrjbut'ing d'irect drainage runoff to the lake.

Modifications of the sept'ic tank proce.dures were made for Butternut Lake,

Moss Lake, Elk Lake and Enterprise Lake. At Butternut Lake, the large number of

resorts (e'ight) suggested that some were year-round, therefore 50 percent were

treated as year-round occupancy. For Elk Lake all seven dwellings vrere assumed to

be year-round res jdences due to their proximity to the Town of Phil'l'ips. A

faiiure rate of 3 percent was used for calculating sept'ic tank loadjngs to l4oss

Lake. Since Enterprise Lake was chosen to estimate the impact of septic tanks,

septic tank loadings were estimated for what were considered the most probably

conditions. Langlade County, in which tnterprise Lake is located, is estimated by

county sanitary code administrators to have a 3 percent septìc tank failure rate,

although sanitary surveys of private seu¡age disposal systems serving waterfront

properties around 13 l.lisconsin Lakes showed failure rates averaging 22 ta 26

percent (l^l.N.R.8.,1977). These surveys also'indicated that 70 percent of the

properties were occupied seasonaì1y. Based on these considerations, 50 percent of

the dwellings and the camp were consjdered to be seasonal, and a septic tank

failure rate of 3 percent was used.

-c1,2-

APPINDIX D

l. Precipitatìon, Runoff Rates, and Land Use Areas forTest Lakes.

2. Phosphorus Nutrient Loads for the Test Lakes

Table D1: BaIsam Lake precipitation and runoff (cmlyr)

Dry Avg. WetYear Year Year 1978 19BO 1981 1982 (Ð

Precipitation (b) 54.1 74.9 114.5 BO.0 80.2 77.2 7B.q

Runoff (c) 16.3 26.7 38.B 28.3 28.4 27.4 27.8

(a)

(b)

(c)t

Table D2:

Source

7982 data were used for January through August, anda\¡erage year values (NOAA) for the remaining months.The average year value is for the lake location(NOAA climatological reports). The dry and wet yearvalues are Chippewa River Basin averages (young andHindall, I972).These âre calculated estimates for the lakeIocation (see Appendix C).

Balsam Lake runoff rates (cu m/s) (a)

1978 1980 1981 19A2

Direct Drainage

Birch Lake InletMud Lake Inlet

o.086

1.481

o.016

0.086

1.486

0.016

0. o83

1.434

o. o16

o. oB5

1.454

0.016

Total 1.583 1. s88 1.533 1.555

(a), Lake surface areas were considered to have zer^onet yearly runoff.

-D1-

Table D3: Baisam Lake

Categorv

land use areas.

Area( sq km)

%ofCategory

Area

Direct Drainagea. Marsh and Swampb. Forestc. Agricultured. Shoreline R.esidental

3.44.31.8o.1

35.444. I'18. I

1.O

tvlud

Subtotal:

Lake Inl-eta. Mud takeb. Marsh and Swampc. Forestd. Agriculture

9.6

4.20.t1.2o.5

100. o

1.0. o5.O

. 60.o25. O

Bircb Lake Inlet

Balsam Lake

Subtotal: 2.O

165

1.1

100. o

100. o

Loo.o

TotaI 178

-D2-

Table D4: Butternut Lake precipitation and runoff (cm/yr)

Dry Avg. WetYear Year Year 1978 1980 1981 1982

Precipitation (a)

Runoff (b)

54. 1 e3 .7

15. 7 30.8

83.9 90.0 75.7

30. 9 32.9 26.3

114. 5

40.6

(c)

(c)

The average year value is for the lake location(NOAA climatological reports). The dry and wet yearvalues are Chippewa River Basin averages (young andHindalI, i-972).These are calculated estimates for the lakelocation (see Appendix C). :

1"982 precipitation data were not available from thePark FaIls station.

Table D5: Butternut Lake runoff rates (cu m/s) (a).

Source l97B 1980 1981 79a2

(a),

(b),

(c),

Direct Drainage

Spiller Creek Inlet0. o83

o.204

o. oB9

o.2t7

o. 756

o.o47

0.071

o. 173

0. 605

0.037

(b)

(b)

(b)

(b)

Butternut Creek Inlet 0.71O

Schnur Lake Inlet o.044

Mud Lake Inlet 0.036 O.O39 0.031 (b)

TotaI 1.o77 1. 148 0.917 (b)

(a),

(b),

Lake surface areas werenet yearly runoff.:-.9BZ precipitation datathe Park FaIls station.

considered to have zero

were not available for

-D3-

Table D6: Butternut Lake land use areas.

Area%of

CategoryÀreaCatecror

Di recta.b.c.d.

km

DrainageMarsh and SwampForestÀgricultureShoreline Residental

1.43.42.9o.B

16.540. o34. 19.4

2.7¿+.551 .42r .6

Subtotal:

Mud Lake Inleta. Mud Lakeb. Marsh and Swampc. Forestd. Agrl.culture

8.5

o. l_

0.9t_.90.8

100.0

Schnurct.b.c.d.e.

Subtotal:

Lake InIetSchnur LakeMarsh and SwampForest *''

AgricultureShoreline Residential

3.7

0.60.62.5o.6o.2

100.0

13 .313 .355.713 .34.4

Subtotal:

Spiller Creek Inleta. Marsh and Swampb. Forestc. Agriculture

4.5

7.35.97.6

100.0

3s. 128.436.5

Subtotal:

Butternut Creek InletButternut Lake

20.8

72.5

4.0

100.0

100. 0

100. o

TotaI LL4

-D4-

Table D7: Elk Lake precipitation and runoff (cn/yr)

DryYear

Avg.Year

WetYear 19 7B 1980 1981 r9B2

Precipitation (b) 54.L 85.2

Runoff (c) i-5.3 31.0

114. 5

40.3

84.9

30.8

87 .7 77 .5 83.1

31. B 26.6 29.8

1982 data \,/ere used for January through Augnrst, andaverage year values (NOAA) for the remaining months.The average year value is for the lake location(NOÀA climatological reports). The dry and wet yearvalues are Chippewa River Basin averages (young andHindal], 1972).These are calculated esti-mates for the IakeIocation (see Appendix C).

Table DB: Elk Lake runoff rates (cu m/s) (a)

Source 1978 19BO 1981 19A2

(a),

(b),

(c)t

Lake Duroy InletDirect Drainage

4.268

o.037

4.406

0.038

3. 686

0.032

4.729

0.036

TotaI 4. 305 4.444 3.718 4. 165

(a), Lake surface areas were considered to havezero net yearly runoff.

-D5-

Table Ð9: Elk Lalce land use areas.

AreaCatesorv (sq km)

%afCategorlt

Area

Direct Drainagea. Marsh and Si*ampb" Forestc. Agricultured. Urban and Airport

o.3o.71.L7.7

7.918.428.944.8

Subtotal;

take Duroy InletEIk Lake

3.8

437

o.4

100, o

100. o

100. CI

TotaI 441

-D6-

Table D10: Enterprise Lake precipitation and runoff (cm/yr).

Dry Avg. WetYear Year Year 1978 1980 19q1 1982 ( a)

Precipitation (b) 60.2 76.3 1O1. B 101.4 81.4 72.6 75. O

Runoff ( c ) 19.3 32.O 48.6 48. 3 35. 1 28.B 30. 9

(a) r l9B2 data were used for January through August, andaverage year values (NOAA) for the remaining months.

(b), The average year value is for the lake location(NOAA climatological reports). The dry and wet yearvalues are Upper Wj sconsin River Basin averages(Oakes and Cotter, 1968).

(c), These are calculated estimates for the lakelocation (see Appendix C).

Table D11: Enterprise Lake runoff rates (cu m/s) (a).

Source 1978 1980 1981 1982

West InIet o. o44 0.o32 o.026 0.028

Direct Drainage 0.167 0. L21 O.099 O.1Oz

TotaI o.211 0.153 0.125 0.135

(a) r Lake surface areas were considered tohave zero net yearly runoff.

-D7-

Talrle ,D72¡ Enterprise Lake land use areas.

T" afArea Categrory

Category {sq km) Area

Direct Ðrainagea. Marsh and Swampb. Forestc. Agricultured. Shoreline Residential

2,67.7o.3o.3

23.970.72.72.7

Subtotal:

West Inleta. Marsh and Swampb. Forest

10. 9

L.91.0

100. o

65.534. s

Subtotal: 2.9

1.9

Loo. o

100. oEnterprise Lake

TotaI 15. 7

-D8-

Table D13: Moss Lake precipitation and runoff (cn/yr).Dry Avg. Wet

_ Year Year year 1978 1980 1981 1982 ( a)

Precipitation (b) 54.1 82.2 114.5 93.6 77 .3 69. O 81.9

Runoff (c) 22.6 33.4 44.9 37.6 30.4 25.6 33.2

(a), i-9B2 data were used .for January ti:rouqh Auqust, andaverag:e year values (NOAA) for the remaininq. months.

(b) t The average year value is for the lake 1ocation(NOAA climatological reports). The dry and wet yearvalues are Chippewa River Basin averages (young and.Hindall, !972).

(c) t These are calculated estimates for the lakeIocation (see Appendix C).

Table D14: Moss Lake runoff

1 978

rates

1980

(cu m/s)

19Bl_

(a).

1982

Direct Drainage 0.036 o.o29 o.o24 o. 031

(a)t Lake surface areas v/ere considereA to .hãvezero net yearly runoff.

Table D15: Moss Lake land use areas.

%ofArea CategoryCategorv (sq km) Area

Moss Lake

Direct Drainagea. Marsh and Swampb. Forestc. Agricultured. Shoreline Residenti_ale. Urban - Residentialf. Wastewater Lagoon

Subtotal:

o.B

o.52.to. Lo.1o.1o.1

100. o

16. B70. o3.3J.J3.33.3

3.O

Total

-D9-

3.8

100.0

Table D16: Swan Lake

DryYear

precipitation and runoff (cn/yr).

Avg. WetYear Year 1978 19BO 1981 I9B2

Precipitation (b)

Runoff (c)

78.0 113.4 96. 1

18.B 35.4 26.7

103 .5 83 .9 81.6

30.3 2I.2 20.3

48.3

11.4

(a)'

(b),

I9B2 data were used for January through August, án¿average year values (NOAA) for the remaininq months.The average year value is for the lake location(NOAA clj-matological reports). The dry and v¡et yearvalues are Fox-WoIf River Basin averages (Olcott,1e68).

(c), These are calculatecl estimates for the lakelocation ( see Appendix C) .

Table D17: Sv¡an Lake runof f1978

rates

1980

(cu m/s)

L9B1

(a).

t982

Fox River InletDirect Drainaqe

I.245

o. 1BO

1.4J.2

o.205

O.9BB

0. 143

0.946

o. 137

Total: 1 .425 I.677 1. 131 1.083

(a) t Lakezero

surface areas \^¡ere considered to havenet yearly runoff.

Table D1B: Swan Lake Land Use Areas.%of

Area Category94tegory (sq km) Area

Swan Lake

Direct Drainagea. Marsh and Swampb. Forestc. Agricultured. Shoreline Residential

Subtotal:

Fox River Inlet

1.6

5.12.7

13 .0o.5

100. o

24.O12.761. O

2.32t.3

r47

100.0

100. o

Total

-Dt_o-

170

Table D19: Townline Lake precipitation and runoff (cn/yr\ .

Wet Avg. DryYear Year Year 1978 19BO 1981 1982 ( a )

Precipitation (b) 60.2 76.3 101.8 101.4 81.4 72.6 75.O

Runoff (c) 20.t 26.2 40.8 40.6 28.9 Z4.B ZS.7

(a), l-9B2 data were used for January through August, andaverage year values (NOAA) for the remaining months.

(b), The averag'e year value is for the lake location(NOAA climatological reports).. The dry and wet yearvalues are Upper h¡isconsin River Basin averages.(Oakes and Cotter, 1968),

(c)t These are calculated estimates for the lakeIocation (see Appendix C).

Table D2O: Townline Lake runoff rates (cu m/s) (a).

Source 1978 1980 1981 7982

Townline Creek Inlet O. 109 0.078 0.067 O. 069

Direct Drainagie o.o22 0. 016 0.013 0. o14

Maple Lake Inlet O.O21 O.O15 0.013 0.013

TotaI o. 152 0. 109 0. 093 0.096

(a) r Lake surface areas t{ere considered to have nonet yearly runoff.

-D11-

?abLe D2!: Townline Lake land use areas.

AreaCategory {sq km)

%arCategory

Area

Townline Lake

Direct Drainagea. Marsh and Swampb. Forestc. Agricultured. Shoreline Residential

0.6

4.21.10.3o.1

Subtotal I.78.5

1.6

lownline Creek

Maple Lake Inlet

Total 12 .4

-Ð12-

Ìäblè D2?: Balsam Lakë Phosphorus Loads.

1 978 1978 Chanoe ln I oael!.¡ í th Der . P W,i thour Der . p

Yo ot' %sr %aîTÖra I W¡r,hgource

, - , kq/yr Tota I kg¿vr. .T.otã I ,-ko/,.vr Det. p

D i rect Dra i nagea. Marsh and Svampb. F0restc. Agrieulture

,5?A45 1 0ûtt9 1 O

'55 245 'l

45 1

10(â) <r

d.. shó re t i ne Rgg,i.den r ia t, . =5 <'! ., 5 <1 -" 0 gsubtotât! t5o 5 150 5- E

Atmospherie 20 I 2A 1 0 O

sépt ¡c Tãnks B(a) <1 2 <1

tlt"JTP (10020 renoval) 0 0 O 0 0 O

Tributariesa. B i rch Lâke I n I êt 300CI 93 3000 93 0 0þ,_¡rttd__te_tse_-!,r'let _. .l+0 1 tp 1 _ 0 0Subroral: 3040 9q 3040 947

Tota I 3220 100 3218 100 <1

(a): Th¡'s valuethe sept ¡c

\{as not rounded off in order to shûw the magnit,ude oftank/t.i le f ield phosphorus load.

-01 3-

Table D23: Butternut Lake Phosphorus Loads.

1978 1978With Det. P W¡thout oet. P

Chanoe in Load

Sou! ce%sî

ka lvr Trrtá Ill' af %of

Tota I HÍthko/vr Torå I kc /vr Dêr - P

Di recÈ Dra inagea . l4a rsh a nd 9wa mpb. Forestc. Agrículture

AÈmosphe r i c

Sept'i c Tân¡(s

WWTP (20l¿ removal)

Tributaries:a. Spiller Creek

1r2(a) 4 Bo(a)

480 19 340

390 16 390

3520015 10075300

300332 1

15 140 6

1700300

35 1

15 1

753d. thoreline ResidentiaI 'l 5_ 1 _ 15- J 0 0

SubrÖtal; 1t{0 é 140 7 O O

70

b. Schnur Lake ¡nfet 70 3 70c. Mrrd Lako lnle¿ 70 370300d. Butternq! creek '1130 .46 1130. ¡{9 0 0

Subrota l: 1660 68 166A 72 o o

Tot,a I 2462 10Õ ?294 100 170

(a): This value was not rounded off ¡n order to Ehow the magnit,ude of theseptic tânk/tile field phosphorus load.

-014-

Táble DZq: Elk Låke Phosphorus Loads.

1 978 1978I.l¡rh, Der.P. l^tithour Der-.P

%ar %or

Chsnoe in lo:ar.l

%orToral þlithSource Rãlvf Tot,a I ko./vr Totâ I kolvr Det- P

Direct Drâ inagtsa. Marsh and Swamp 5b. Forest 5c. Agriculture 30d- Urban & Airoort- lg0

0ooll

000o

<'f 5 <1<15<1<ì 30 <'l215û3

subt,ot,a l:Atmosphê r i c

Sept ic Tanks

HWTP: ( ?0% rernsva I l

Lakê ûur.öy lnlet

2.30

5

4(â )

1 660

574CI

230

5

3,(a )

1 170

5740

3

<1

<1

22

75

0

o

'l

490

0

0

o

<1

6

0

3

<1

<1

16

80

Totå I 7639 't 00 71tr8 100 491

(a): This value waôof the septic

not, ru¡unded off in ordertank/t i le f iald phoÊphor.us

to shov theloâd.

magn i tude

-t15-

Table D?5: Énterprlse Lake Phosphorus Loads.

1978l4.Lrh Der. P

o

source kq/vr Y;"iït ko/vr 7i"?[,

1 978H¡thout Det. P

Chànde f n.lr¡âd

%a¡Tota I W¡th

kø lwn llat P

Di rect Dra inageâ. Shorel inë Marshe$b. Forest

At-mosphe r íc

sept ¡c Tanks

West lnl6t

37 1CI0 38006 15 6 0

35 13 0

zr(â) 1o

80 31

1ûO15

c. Agriculture 0 0 O 0 0 0d. Shgrgline,ResidÉnríal ==? ,2 ..1 ? _ O Osuþrorati 120 44 12Q 46m35 't3

35(a ) 13

80 30

104o0

Totå I 270 100 260 100 10

(â): This valuethe sept¡c

vas not rounded off in order to show the mâgnit,ude oftaîk/Ei le field phosphorus load.

-D't 6-

Table 026: Moss Lake Phosphoru( Loads.

1978 1978with oet. P }.lírhour, Der. P

loof %af

Chânûè ln I oecl

%arTotaI Hith

D¡ rect Dra i nagea. Mn rsh and Swampb. F(rrestc. Agricult¡.rr€d. urban * RÊs¡dential

Atmosphe r i c

Septic Tanks

WWTP ( Lagoon)

10 16'r0 1600

10 16

'¡0 17 0 010 't7 0 00000'¡0 17 0 t

15260CI8(a) 1I¡ 4 6

0000

- e. shorelíne Rêsidential ã I t 9 0 0'

't5 ?,12(a ) 19

00

Tot,a I 10058ro062

(all lhis value wasseptic tank/ti

not rounded off ¡nle field phosphorus

order to show the magn¡tude of theload-

-D1 7-

Table 027¡ Swan Låt(e Phosphorus Loads.

1978 1978 Chanoe in Loadìrt¡rh qer. P }lirFo,r¡ü CIer. p

lj, kolvr t"¡äl.i;'n

Di rect Dra inage

Atmosphe r i c

sept ic Tanks

WwrP (aO% remova I )

Fox River lnler

320 7 320

30130I'l

44(a ) 1 31(a) 1

1730 39 122û

235ø 52 23tO

3-1

,9

0

0

13

510

0

0

o

<l

11

o

Tota I 447t4 100 39>1 100 12523

(a): Thls valuethê sept¡c

lras not rounded off ín order to shov the nagnituds oftan\/t í le field phosphorus load.

-D18-

Tâble 028: Townl ine Láke Phosphorus Loads.

1978W ¡ th Þet,, P

/ø of

19781,ri t.hf)rrt Det - P

chãnoe ln Load

l" of Y, ofTorâl Hith

Soqrce ko/yr TotäI ,lql.vl: TotåI .,.-._Fq,/yf. pet. F

D ¡ rect, Dra í nageâ. Marsh and gvampb. Forestc. ÂgricuJ turèd. shorel¡ne Rrel¡ne Residential 5

555

<1<1<1<1

5<to5<'t05<1 CI

5<TÖ

00oo

Subtota l:Aümosphe r i c

Septiç Tanks

WWTP (20% remova f )

Trlþutaries:a. l-vlaple Lake lnlet

20

10

30(a)

54

23

o

o

1

2

2

2

3

6

3

2

4

I

20

10

21(a)

38

25400

0

0

9

t6

Tota I

b. ]'ovnl ¡ne e"reek Þ?0 79 . ..520 82 0 Osubüora I r 545 83

'45 86 0 0

699 't00 100 2'ó3lr

(a): Th¡s value vas nÕt rounded off ¡nseptic t"ank/t,i le f ield phosphorus

order to shov the m.âgn¡tude of theI oad.

-019-

APPINDIX E

Temporal Variations in Total Phosphorus Concentrat'ions,

Chlorophyll a Concentratjons, and Secchi

Disc Depths in Study Lakes

Iable El: Hean pre-ban and post-ban total phosphorus concentratjons, chlorophylì a concentraticns, and Secch'i disc depths for LittleBearskin Lake and its test lakes: Enterprise, l'loss, Swan, and Townline Lakes.

Pre-ban Ban

7978 r.980 i981 1982 1 980 - 1982Lake (lest/ % Change "l Change % Change % Change. -nãrå.ãr.ål pareameter Mean(ts.d. ) Mean(:s.d. ) f;o; t9i8 Mean(ts.d. ) i.om réie Mean(=s.d. ) rro¡r tgTg Mean(ts.d. ) rrom tdze

Enterprise Total P(ug/L) 23.0(19.8) 48.s(t32.0) +111 74.8(:68.0) +??5 47.3(:28.4) +!06 5q.1(t41.q) *l1s(reit) chlorophyit a (us/L) 10.0(16.0) 14.6(:13.9) +46 14.1(114.9) +41 i6.9(:15.1) +69 15.3(t13.9) +53'

secchi disc ãeptñ (m) 1.9(i0.6) 2.1(:0.3) +11 2.6(t0.9) ,37 2.0(:0.8) + 5 2.2(,tA.8) +L6

Moss {Test) Total p (us/t-) 26.4(t8.8) 33.8(:26.2) +47 49.2(t?0.7) +85 22.0(:13.i) -17 35.9(t22.4) +36

Chlorophvli a (uslL) 6.a(r2.8) 6.3(t2.8) - 2 5,7(t3.4) -11 6.7(22.6) + 5 6.3(t2.8) - 2

secchi disc îeptñ (m) 2.6(.0.5) 3.3(10.9) +27 3.7(10.9) +42 3.5(:0.8) +35 3.5(t0.8) +35

Swan (Test) Tatal P (us/L) 77.4(t35.6) 87.9(:44.3) +14 68.6(ti6.8) -11 54.4(i-î5.1). -30 69.5(t35.!) -iqchlorophyìí a (ug/!-) 23.6(i18.3) 29.6(:31.3) +25 37.L(x26.9) +57 20.1(:13.16) -15 28.5(t24.2¡ +27

Secchi dìsc ãeptñ (m) 1.9(t0.9) 2.2(t0.9) +16 1.8(10.8) - 5 1.7(:0.6) -11 1.8(:0.7) -5

Townline (Test) Toral p (ug/L) 59.8(123.9) 6I.4(=32.2) + 3 51.6(t10.9) -i4 47.4(:27.3) -21 53.?(t?4.6) -i1ChlorophylÍ a (ug/L) ?I.3(t9.7) 22.2(=L0.8) + 4 22.0(t8.7) + 3 14.6(t1C.8) -31 19.3(t10.3) - 9Secchi ¿isc ãeòtñ (m) i.0(:0.i) t.s(:0.3) +s0 1.7(t0.s) +7a 2.0(10.9) +100 1.7(10.6) +70

Li tt] e Bearski n(Reference) Totaì P (uslL) 33.7(t3.6) 49.3(:32.8) +46 si.5(t25.4) +53 42.4(:22t2) *4q 47.5(t22.0) *41

chlorophyli a'(uq/L) i4.6(r7.0) 72.7(:6.4) -13 15.5(t10.5) + 6 72.6{t9.2) -i4 13.5(:8.5) - 7

secchj'oisc dept¡r (ir) 2.1(10.4) 2.6(t0.9) +24 2.3(t0.6) +10 ?.7{=A.6) +?9 2.5(10.7) +i9

Note: 1) Annual means are averages of monthly means of each year's sampling program: average of Sites 1 and 2:. 1978(N=6), 1980(N=6), tSStlt't=01, 1982(N=7), 1980-81(N=i9).

2) s.d. = standard deviation.

-El -

Tab'le E2: l.lean pre-ban andfor Teal Lake and

post-ban tota'l phosphorus concentrations, chìorophyllits test lakes: Balsam, Butternut and Elk Lakes.

a concentrations, and Secchi dÍsc depths

Pre-ban Ban

Lake (Test/Reference )

Notes:

Footnotes:

1978

Mean(ts.d. )

41 .3 (r16 .9 )2?.5(tt3.2)1.8(10.6)

60.9(r29.3)27.6(t28.1)1.1(t0.6)

72.4(t18.2)7.4(t2.7)0.7(t0.2)

1982reMean(ts.d.) from 1978

1980-i982'1 Change

Mean(ts.d. ) from 1978

' /r \

7t-7(t85.5)(oJ +7420.3(tiz.4) -i02.2(t0.6) +11

Mean(ts. d. )

127.8(i139.0)(a)25.8 ( t19.0 )2.a(=0.5)

77.8(t2i.1)27.8(t2t.4)i.5(t0.4)

6I.7 (t27.9\ie.0 ( t8.2 )

1.2(r0.3)

se.z(tr¡g.s)(c)20.3 ( r18 .2 )2.4(10.9)

1980rel4ean(ts.d) from 1978

1 981

Balsam (Test) Total P (uSiL)Chl orophyl 'l a ( ug/L )Secch'i djsc î'epth (m)

Butternut (Test) Total P (uSlL)Chlorophyll a (us/L)Secchi djsc -depth (m)

Elk (Test) Total P (usll)Chlorophyll a (uS/L)Secch'i djsc -depth (m)

Teal (Reference) Total P (uslL)Chlorophyll a (us/L)Secchi disc ðepth (m)

Pa rarnete r% Change

from 1978

+209+15+33

+28+1+Jb

-15+157+7t

+¿ól+50+26

48.?(t29 .7 )1"8.4(t14.5)2.a(to .7 )

76.7 (t34.4)23.7 (xL7 .t)1.5(t0.6)

80.9(t27.4)28.3(t29.s)0. e (r0.3 )

47.5(r36.5)13.2(is.8)2.8(11.2)

+t7-18+33

+26-14+36

+12+?82+29

+84ô

-L+47

43 .7 (t22.3)13.9 ( t10.3 )2.0(t0.4)

65.0(t25.5)27 .2(t25.1)r.3(t0.2)

+6to

+11

fJö

+18-5

+19-5+¿/

-10+178+57

+1?9+?1lLl

54.31116.9)15.5(r12.1 )t.2(t0.2)

+7 72.7 (t26.5)-1 26.3(t20.5 )+18 1.4(t0.4)

-25 65.0(r23.8)+i09 20.61t18.4)+7I 1.1(t0.3)

35.7 (t23.3)i5.9 ( t9.6 )1.8(r0.5)

25.9(t3.8)13.5(t7.6)1.e(t0.6)

ss.+(tez.z)(d)16.4(t11.9)

2 .3 (t0.9 )

i)2\

(a)

(b)

(c)

Annual means are averages of monthly means of each year's sampìing program; average of sites1 and 2: 1978(N=6), 1980(N=6), 1981(N=6), 1982(N=7), 1980-82(N=19).s.d. = standard deviation

(d)

1981 Mean is 71.9(x27.4), +74L, without exceptionaììy high value from thesamp'l i ng date i n 1981 .1980-82 Mean is 53.0(:27.6), +28%, without except'ionaìly h'igh value fromsampling date in 1981.1981 Mean is 41.9(t15.8), +6?%, without exceptionally high value from thesampf ing date in 198.l.1980-82 Mean is 41.4(125.9), +60%, without exceptionally hìgh value fromsampling date in 1981.

I ast sunrmer

the I ast surnmer

'I ast sunrner

the last sufimer

C'

FIGURE E'IA: TEMPORAL VARIATION OF TOTAL PHOSPHORUS INS!'JAN AND LITTLE BEARSKiN LAKES.

LITTLE BEÊR SKIN LÊKE ffiEFERENCE)

r9?8 1979 1980

JE(5(-)HE

J

=(.}CJHE

J F ]t ß N J J R S O N O J F II R II J J R S O N O J F N Ê ñ J J Ê S O I{ O J F I1 R I1 J J R S O T{ D J F ñ R N J J ß S O N O

-E3-

t38t 1982

('tN(fIaþta

TñãIrHv,r¡3'tl¡

TPC¡f{

zoIc¡.Þå

FIGURE EIB: TEMPORAL VARIATION OFENTERPRiSE, TOWNLiNE,

TOTAL PHOSPHORUS iNAND LITTLE BEARSKIN LAKES

ENTERPRISE LÊKE

J

õs(JHE

J

()õ(JHE

JE-(-)E(JHE

EHI LITTLE BERR SKIN LRKE (REFERENCE)

!+.€Es4s

1378 l9?9 1980 l98l

TOi,INLÏI{E

JFNRNJJÊSONDJFIIÊIIJJÊSOI{DJF11ÊIlJJRSONDJFNSñJJRSOT'IDJFñf,I1JJÊSOND

-E4-

1982

F I GURE ElC: TEMPORAL VARIATiON OF TOTAL PHOSPHORUS IN

MOSS AND LITTLE BEARSKIN LAKES.

cñl\,ülctC.:ctTñIrHtnrl3tt-llI

.oC'.1z.oIÞul

JE-(J¿5(JHE

JE-c3ãL)HE

EH¡ LITTLE BERR SKIN LRKE (REFERENCE)

E€Eees

J F N Ê lt J J R S O N O J F I'I R 11 J J ß S O N D J F ñ R N J J ß S O N D J F N Ê N J J Ê S O I{ O J F N R N J J R S O N O

t980

-E5-

G'

t97B l97g l98l 1382

('tr\,d)ctc¡@

TnãIrHanr¡ôttl¡

fF.1z.G'

Ictl\)(o

F I GIJRE EI D: TEMPORAL VARIATION OF TOTAL PHOSPHORUSBALSAM, BUTTERNUT, AND TEAL LA}(ES.

A

EJTTERI{UT LTìKii

t980

-E6 -

I l.¡

J

äa(JHE

_tE^(JE

,L)HE

J

EsL)HE

(Þ*--s

flnl

J\lô

t\t\

LJ\

J F rl fi ñ J J R S O|t 0J F n R n J J Ê S 0 N D J F n n n J J R S 0 N 0 J F n R n J J Ê S 0 il D J F l1 I ll J J ß S 0 H B

j

#i

t978 1979 lgSt t982

fjt l

'\']g¡c,ñ,

'oqtrHU'f't,llI

TCI

C]

IG¡Àjg¡

FiGURE EIE: TEMPORAL VARELK AI'ID TEAL

IATION OF TOTAL PHOSPHORUS iNLAKES.

J

ËaL)HE

J

õ=(JHE,

,d-J\ F,U\

b

0*1b

"Jf

(}----<Ð ELK LSKE

t9?8 1979 1980

REFERENCE)

J F T1 R II J J R S O N D J F 11 H N J J R S O N D J F N Ê ñ J J Ê S O T{ O J F I'I F 11 J J R S O N O J F N Ê ñ J J R S O N D

-E7 -

t98r 1982

FIGURE EZA: TEMPORAL VARIATION OF CHLOROPHYLL A I

SWAN AND LITTLE BEARSKIN LAKES.

EHI LTTTLE BEÊR SKIN LRKE (REFERENCE}

c3J F n AH J J â S 0 N D J F il  n J J-á S 0 N 0 J F n Ê ñ J J ß S 0 t{ D J F n R H J J Ê S 0 il D J F l',l R t1 J J A S 0 N 0

l9?9 1980

N

rd

4'

V

?il

/\[

\/

H(/ilf\t I<')lc)tc¡)lÀ)I'l'91nãtrHU,rlG'

tlt.oCl,+z,oI(Þl\'

JEg=(JHE

t978

-EB.

tg8t 1982

FIGURE E2B: TEMPORAL VARIATION OF

ENTERPRISE, TOWNLINE,CHLOROPHYLL -A INAND LITTLE BEARSKIN LAT'ES

ENTERPRTSE

TÛi]NLI}'JE

(,rlf\tg,oò.DaIrHU'lloll¡

.uCl.4

oIt3(¡

JEq€L)HE

EH¡ LITTLE BEÊR SKIN LRKE REFERENCE)

eJ F N R N J J ß S O T{ D J F II Ê N J J Ê S O T{ O J F N R ü J J ff S O N I} J F N R fl J J ß S O N O J F 11 R II J J Ê S O N O

r9?8 1979 ì980 1981- -rn-

1982

(,tf\Jo)c¡('lCt¡

¡0f!

Irt-{<ttflø.F.ñI.:-.gtiClt

c¡¡c!(¡).(¡¡

JEO.€L)

HE

o

F I GURE TZC: TEI,,lPORAL VARIATION OF CIJLOROPHYLL A INMOSS AND L]TTLE BEARSKIN LAI(ES.

EHI LTTTLE BERR SKIN LÊKE (REFERENCE)

J F n R I J J ß S 0 N D J F ll R n J J ß S 0 }{ fl J ii' n ß n J J ß S 0 N 0 J F tl Ê n J J R S 0 N 0 J F ñ R n J J â S 0 N D

r980

-El 0-

r978 r97g t98t tg82

(,tl\,o)c¡g,(n-¡}ftÞIrHU'r¡¡tIt¡

t('?+

zc¡IÞ

FIGURE EzD:. TEMPORAL VARiATIONBALSAI4, BUTTERNUT,

OF CHLOROPHYLL A INAND TEAL LAKES.

ÊUTiËR*JIJÏ

JFñRNJJÊSONOJFHRNJJRSONDJFNgNJJRSONOJFNRNJJRSO}IDJFNRñJJRSONDt

t97B l3?gl 1380

-Ell-

198t 1982

F i GUR.E EZE: TEMPORALELK AND

VARIATION OF

TEAL LAKES.CHLOROPHYLL A IN

i

I

Ii

I

-Åï:p.'dt-)HE

H ELK LÊKE

C:¡

JFñRNJJRSO.NDJFIlßIlJJÊSONOJFIIÊIIJJRSONDJFItÊIlJJÊSOI{OJFIIÊNJJHSONO

1979 1980

ril

I

,l

å--oanIÀ)IcDlcrl{tàl'lTI'rt I

=ltlf-HU'r¡ot-ft¡

'gc!ñzC¡

I@À)Cl

JEqç(JH=

1978

-812-

r98l 1982

FIGURE E3A: TEMPORALSWAN AND

VARIATION OF SECCHT DISC DEPTH INLI TTLE BEARSK I N LAKES .

l-llle'¡l.l-1l.

UTÌ\)ac,@\¡!ñ5I

Iq

anÍtotl-flI

.pêèzoå9'

EHI LITTLE BERR SKIN LÊKE ffiEFERENCE)

t-[Uc¡Lrl -LL Ltu/k

1980

-El 3-

J F N R N J J fi S O I{ D J F 11 A TI J J Ê S O H O J F È' R II J J Ê S O II O J F N Ê ñ J J Â S O T{ D J F N Ê il J J Ê S O N O

1978 1979 r98r lg82

FIGURË E38: TEMPORAL VARIATION OFENTERPR I SE/ TOWNL I NE,

SECCHI DI SCAND LITTLE

DEPTH INBEARSKI N LAKES

t--uouJ-LJ.

t-Irlotrl -tl-

s----s TÛ'J|'ILINE LfrKE

EHI LITTLE BEÊR SKIN LÊKE (REFERENCE)

¿nINri9lè.à-oñtt-HîJ,nt¡Fft!

.EÞ-f'.+zo,ct

CÐl\)

FLLlotr¡ -tJ-

æ*gr€b

t980

-El 4-

1981 1982

ENTERFRT$E

.&* þ n/juó

Utu/hJ F N R N J J Ê S O N I¡ J F 11 ß N J J R S O N O J F ñ R N J JÂ S O N O J F TI Ê 11 J J R S O Ì{ O J F il R N J J ß S O il D

t978 rg79

qlt\tq)Cf(o

TlltIrHaclo¡r-,tI

Eê.+z.Ct

tc,o(3

F I GURE t3C: TEI"lPORALMOSS AND

VARIATION OF SECCHl DISC DEPT}J INL I TTLE BEARSK I I.I LAKES .

Flllertr, *t!

EH LITTLE BERR SKIN LÊKE (REFERENCE)

t-[Ilcrtr-l -U- Ltu/h

1980

-El 5-

J F ñ R N J J R S O N O J F 11 ß N J J f, S O I{ O J F 11 ß II J J R S O N O J F N Ê ñ J J R S O H I} J F N 8 N J J R S O T{ O

r978 t979 t98t t982

FIGURE E3D: TEMPORAL VARIATIONBALSAM, BUTTERNUT,

OF SECCHI DISC DEPTH iNAND TEAL LAKES.

l-LrJ oLLJ -LL

F-L¿Jo

-,u-¡-LL

ultNIollÀ)Ic¡l;lnl:tlt1f-Hv,ftûlt!I:TCltz,t¡¡(5l\)C')

t--I r l(=l!*tr-

oJFNRËJJÊSOHOJFTlÊIlJJRSOTIDJFIIRIIJJRSONDJFITÂIIJJRSOI{OJFItRñJJßSO}IO

t978 rg79 1980

E.lITFt',ilJT

\* -,\*þ ry

-El 6-

198t 1982

FI GURE E3I: TEMPORALELK AND

VARIATION OF SECCHITEAL LAKES.

DISC DEPTH IN

FIl.lc>

L¡-

uttl\'I\¡lÀJlool;lrtl5ttlËt'lültctlo1F-lÀlI

tÞ-ÞÉ2ÈtÊ¡

t--[rJorJ-l-L

€JFnßnJJss0NDJFnRñJJRsoNDJFnSñJJÊsoNDJFnÊñJJRs0t{DJFnñnJJRs0HD

1980

-El 7-

tg78 1979 t98t 1982

Secchi Disc

Rel ati onsh i ps

APPINDIX F

Depth and Chl orophy'll a

in Townlìne and Elk Lakes

sD

T

sc

o r a +. . - . +. . . o + . r . . *. . a . * . . . . *, . . a * - a a a l. . ¡ . f . . . . t. . _ .-a'

'al¡.0 I at

a'.a

a.

J,8 + ;a

3a

a'

-'3.6 + '+

a

.l-' t.a

a'

J.q I r '.+a

.l-' t'aa'

.13.2 + '

+

--a' 'a¡

!3.0 +l t Z I t t Z 1+

a'

.'a

a

2.8 + '.l .-

aa

a'.a

a a.a ?. . . . l. . a . t. . . . I . . . . *. o ¡ r O. . a . l, . . . *. . . . *. . . . l. . - a9. t5 21 21 33-'r2 13 2$ 30 36

CHtA

FIGURE Fl: Townlìne Lake Secchj.djsc depth (ft) versuschìorophyll g_ ( ,g/L) 1978.

-Ft -

..} a . a - i a . . . * r . . . 1 . . - . f - . . . * . . . . 0 a . r a + . . . . t . . a . l a . a . l a

sD

Isc

a

e

I

a

7.2 +

a

t

-a

6.6 +

a

-a'

',6.0 +

e

?

a

t

5.4 +

a

a

t

al¡.8 +

4-2

J-6

a

a

a

+a

a

a

a

+

a

a

t

I

+

a

a

a

a

+

a

a

a

+a

a

a

+

!

a

a

+

a

21

1la

a

a

a

+

Ç

I

a

+

a t.l-r..1. .. .*.. ç..*t. r "*...tf ....*....1. a..1.-..1....{.

5. T5 25 35 ¡t50. 10 50

Townl ine Lakechìorophylì a

30 It0

disc depth (ft) versusI 980.

2A

cü[Â

FIGURE F2: Secch i( ¡gil)

-F2-

:. r..1.... i....Ô.¡¡e *.e ...1....*.._.*..

rt!

8.25 +

.ra

a

7.50 +

-l'.aS 6.75 +

D

1.1src.

6.t0 +1

t ,-.

a

1

5.25 '+

a

.l t I tl1O

a

It.50 +

:a

3.75 +

a

a_

ar aa. f .. ..*a.. - 1... af , ¡..¡}. a _.l. . a. *a...12's 1s.o

l7's 20.o

22'3;r.;'ãz]i"

cHtÀFIGURE F3: Townl ine Lake $ecchi. disc_ depth (tt)chìorophyìì a (-ttgtt)-iõSl.

.. *..o ¡}a...1..

a

a

a

o'o

'!a

a

+

-a

a

-+

a

,a

1-+

l:ttaa

+

a

a

t'a

+

!

aIf

a

ça

1.l. .. . *. . .. l. .

32_ 50.0 .15_ 0

versus

-F3-

sD

rsc

12.25

f0.50

8.7 50

7.000

5.250

3.500

1. ?50

aa

+

a

a

a

a

+

a

a

-o

+

a

a

a

o

a

a

.1a

+

a

a

a

+

a

a

a

a

+

a.

a

a

aa

.*....0.... f a a.. *.... *. t. . t. t t t lt t t t ?.. ' t it t t t *t t t

'a

a

tt

a

a

a

+{l.

a

'a

a

+

a

a

a

a

+

o

a

a

.+o

a

a

I 1.'+a

a

a

a

+

a

a

.a

.*... .*. rt.1.. ..i. ...

2q.5 31.5

1

.1.. -. *. .. . *.. -. *....i....*. ..3.50 10.5

?.00 14.0

FIGURE F4: TownÏ ine Lakechì onophyl 'l g

Secchi disc depth (ft) versus( yg/L) I gez.

17.5

CHLA

2l- CI 28.0 35.0

-F4-

.1 . . . . 0. . . r f .. - a . *. o . . 1 . . . . 0 . . . .1 . . . . * . . . .1 . a . r i ¡ r r . l .aa

_T.0 0

2.75

?.50

z. z5

2.00

f.75

'1.50 $ta

l'¡

-a

+

a

a

a

I

+

a

a

a

I

+

a

a

a

a

+

I

a

a

Ia.

a

a

+

I

I

a

-

2

a

a

+

a

a

¡a.

Ia

a

a'

a

+

a

a

a

a

+

a

a

a

!

+

1+ !

t

a_

+

a

t'

1f

sD

I5c

.'1

a

a

a

a

¡f .o. a{a r ¡ r}c. -. }. ¡ ¡ ¡ I.. a.*....*-... t.,..*.. ,.,}.... $,3. 5. 9. 11

û.

FIûURE F5:

7.

cflLt

6. 8.

tlk Lake Secehi disechlorophyll a ( yglL)

depth (ft¡ versusl g7g,

10 12

-F5-

rtrr.-ti...a

.11û. t¡ +

-t¡.0 +

a

q

3.6 +

a

3.2

a

?.8 +

t

a

2.E +

a

!

?.0 +

a

.*a.. a. *. - a. *. a .a # .. -.*... a{ a.. a}r ¡ or ?. -- . *_

I

a

+a

sD

Isc

:¡a

I

a

c

a

a

+

t

a

t

l

a

a

¡+

a

'I

1.a

+

a

I

a

a

+

a.

e

.l

I

a

+

a

a

o

I

+

.1a

a

a

a

t'

t

a

+

a

.1 11r* ¡ r t'r*r r r r'Fr r '- r *r - r t*t - - -t- -- - *- - - -*- -t -r. t ...*.... *:10. 30. so. --io.--- --.ro:.--0, û 20. 40. 60. g0- 100

CTrLA

FIGURE F6: Elk Lake Secchi disc depth (tt) versuschlor"ophyll a ( "ug/L) lgSO.'

-F6-

6-0. . r +. . . . 0. . a r 0. r . . l a a . . I . ¡ . . *. . . - f . . . . $. . . . + a " . a *. .. -

5.5

5-0

s,D

I l¡.5sc

q.0

3.5

3.0

2*5

+

t

!

a

a

a

I

-+

C

a

a

-+'a

a

a

+

I

a

a

ta

a

e

+

.1a

a

+

at-+r.-¡

6.

l+a

a

a

a

+¡

!

a¡lla

-+

a

l.f

t21 +

"a e

a

elr2+a

a

.!

tt;o

..,'aa'

o1+a

a

a

a2 +''1 . . r . * . . . . f . + . "

.} - . r . *. r , . Ç. . . . f ¡ a . a l. . a . l. .. .!r. 15 21 27 33T2 18 24 l0

FIGURE F7:

CHLÀ

Elk Lake Seechi disc depth (ft) versuschlorophyll g ( N/L) lg8t

-F7 -

.1.... i. ...f .. -.l.. a .*.. .. ta...+.. a. *.... *.. .. i. ...f .

sD

Isc

a

a

a

5.5 ra

a

a

.a

5.0 +

a

a

a

t

Q.5 +

a

I

a

-q.0 +

a

a

a

a

J.5 +

a

o

a

a

3,0 Ia

a

a

a

2.5 +

I

'a

!

a

a

+

a

a

a

e+

t

t

-a

+

a

a

t

o

+

a

a

a

+

a

a

a

t

+

O

a

a

+

i

a

111

.0.. -.*.--.*.. . .*.,.. a|.. ..{... .1....}--..*..5. t5 25 35

.. *....1.rt5

500-

FIGURE FB:

20

CHLå

10 30 t¡0

tlk Lake Secchi discchlorophyll a (¿gll)

depth (ft) versus1982.

-F8-

APPENDIX G

Temporal Variat'ions in Green and Blue-Green A'lgal Counts

APPTNDIX G

Anaìysís of Algal Ident'ification and Enumeration Data

Figures 7A through 7E show the temporal variatjon in green a'lgae over the course of

the study. The monthly means of the counts of green algae are plotted. Fjgures BA

through 8E are s'imilar plots for blue-green aigae. It js read'ily apparent from these

figures that both green and blue-green algae steadily increased in numbers in both test

and reference lakes throughout the study.

Analyses were conducted on logarithm. of.blue greens (1n BG), ìogarithmu of greens

(ln G), p = BG/(BG+G), and ln [pl(t-p)]. The transformations, where used, were for

obtaining better agreetnent with the dìstrjbutional assumpt'ions for the various analyses.

The use of the 'log'istic tnansformat'ion, 'ln P/(1-p), was of narginal value.

Tables l and 2 represent covariance analyses s'imilar to those dc,ne tor total

phosphorus, chlorophy'll a, and Secchi dìsc depth. 0bserve in Table 1, for all

measurements considered, that the apparent track'ing of the test lakes by the reference

lakes is account'ing for a substantial amount of the total varjabilit.y. Even so, except

for the greens, the post-ban effect is statistically sign'ificant (aìthough not

dramatically so). In Table 2, you wil'l observe that this post-ban effect is primarily

assocjated with Elk Lake, with Butternut a'lso appearing for the bìue greens. In both

instances, the direction is associated w'ith increases in the blue greens that were

greater than correspondìng reference lakes.

-G3-

ex

COox

J¿-

frEt-tz.-,

ctx

EHI LITTLE BERR SKIN LÊKE ßEFERENCE'

îd \þ"

J F tI R n J J ß S 0 N 0.r' F n A ñ J J n S 0 il D J F r  rl J J R S 0 il 0 J F H  ñ J J ß S 0 * 0 J F n R n J J F S 0 N D

t978 t979 t980 t98t

FJûURE GJ/\ TEIIPORRL VÊRIRTTON OF GREEN ßLçffE

_Gl _

tg82

JE\ry.a=t-- *H4-J9

x

ê----â EHTERPSTS€ Lffi€

g--.-.q TOJ:.{LiNE LfìKE

Qo

ft{JE

\ou)tl-- -Hz.J9

x

-r+Õix

(oè

et.'ró-'l¿

óóq

\flid tr

ö

JE\ð.u) çF--Hz.ìa

x

wþt978 ts79 1980 t98r ts82

FIGURE G]3 TEIIPORRL VÊRIÊTION OF GREEN RLGRE

Afufl"/{

EHI LITTLE BERR SKIN LRKE ßEFERENCEI

J F N ß N J J ß S O N D J F N ß il J J ß S O N O J F T Ê N J J Ê S O T{ D J F TI ß N J J Ê S O T{ D J F ñ ß N J J A S O }I D

-G2-

JE(nF-Hz.= o

x \n\\r(H I13SS LÊKE

r978 1980 t98t t98?

FIGURE ûlC TEMPORRL VRRIRTTON OF GREEN FLGRE

=G3-

r97e

JFIIRIlJJRSONOJFNÂllJJÊSONOJFTIÊñJJRSO}.IOJFIIRIIJJFSONOJFilßNJJÊSOI{D

!¡(Ðx

lf)E¡x

JE\ñl\Öu)çF--H--)9x

v

ç(ãx

fr}c¡x

J¿-

\o(n7l-- -Hz--J9 x

Ic¡E

(t)IJ!

JE\È(.rît-- -Hz.-rgx

ß--€l EUTTERI{JT LRKT

qEHI TERL LÊKE GEFERENCE)

1978 t979 t980 r98t

FTGURE GID TENPORRL VRRÏRTION OF GREEN RLGRE

-G4-

r1ì'ù)

\eItB-ó-Ð

J F N ß N J J R S O II D JF It Ê N J J R S O }I D J F N Ê ñ J J Ê S O II O J F N R ñ J J R S O N D

1982

H ELK LÊKF

JE\eu)î

t-- -Hz.J9

x

..4ctx

ç¡ctx

JE\Ëu) Ê.t-- -Hz.J=

x

ry'TERL Lf;KE {REFERENCE)

/q

îBÅq F.J\lJ F IT R II J J R S O T{ O J F Tt R N J J R S O I{ I¡ J F TI ß'1 J J R S O N D J F II Ê ñ J J Ê S O N O

1978 r97S t980 t98t

FTGUREG]E TENPORRL VRRÏRTTON OF GREEN RLGRE-G5-

1982

rtc¡x

(l'e

Jç-

fr?Hz,¿el

E

G'ax

JE,

f/)?Hz.-t

Ctx

g---o S'JÊI'¡ LÍIKE A *.4"-f- l\f\ I{\ l*b jòl

ó

EHI LrrrLE BERR sKrN LRKE *EFEREN'Ð f

H f,,fJ\ "r

t982t978 1979 t980 198t

FIGURE G2A TEI1PORRL VRRIRTTON OF BLUE-GREEN RLGRE=G6-

J F fî 8 T1 J J R S O N D J F II 8 ñ J J R S O N D J F ñ Ê N J J R S O N D J F N A il J J R S O TI O J F 11 R II J J Ê S O }I D

tgtx

(t,ctx

(l€x

JEU)F-Hz.=

JxU't-Hz.)

€'{TEf,.ÉßTSE Lfi'.E

ß*"----Ð TÛJI]LINF

t978

/I

T

/

rütò¿

,l\d\tt¿

GHI LITTLE BERR SKIN LRKE ßEFERENCE)

(Ð

=xJE

\oavF.- -Hz.J? x

nÅE/ú

EI

t979 l9B0 l98t

FÏGURE 328 TEilPORRL VRRTÊTÏON OF BLUE-GREEN RLGÊE

t982

JF NR N J J Ê S O N D J F 11 g N J J R S ON D J F Nß ñ J J R S O N O J F NR N J J Ê S O ND J F N Rñ J J Ê S O N O

,G7 -

JËg)Þ-Hz.3

JE\Ë(/|t=F--Hz.-/9 x

ôlc:x

g.--_Ð !1üSS LÊKE

\Å

EHI LITTLE BEHR SKTN LÊKE ÍREFERENTE)þf,'I\ F*l þ dE¡

J F I1 F 11 J J R S O N O J F N R N J J Ê S O il O J F N ß í J J Ê S O N D J F II ß 11 J J R S O N D J F N Ê ñ J J 8 S O N O

ÌC'x

r978 1979 1980 r98t t982

FIGURE G2C TEMPORRL VRRIRTION OF BLUE-GREEN

-Ê8-

!fcl,a

(t¡É¡x

-J4 \õc'Jî

,t-.- -Hz")É

x

.iex

(rtex

-Jr\Õç)Et-- -Hz.J9

x

JE<nt-Hz.)

t978 t97g 1980 t98t 1982

FÏGURE G2D TEIIPORRL VRRIRTTON

T1

ar

\\

\o

BiJïTÊnNL,ï

çox

çtc¡x

$tôx

c¡x

J F N R ñ J J N S O N O J F N Â H J J Â S O N O J F ÌI R TI J J R S O I{ O J FN Ê ñ J J Ê S O N O

-G9 -

OF BLUE-GREEN RLGRE

ELK LÊKE

.('tex

Js-\o(na

t-- -Hz.Jg x

JEat-H4

=

q#"\n:

dÐe,p\

ñ,ox

e,a

TEÊL LRKE ßEFERENCE)

qrruH-Fú\lJ F N R ñ J J ß S O N O J F TI Ê II J J R S O I{ O J F N R ñ J J R S O N D J F T R ñ J J Ê S O N D

t978 t9?9 t980 tg8l 1982

FIGURE ç¿g TEI1P0RRL VRRIRTI0N 0F BLUE-GREEN ßLGRE

-Gl 0-

TABLE Gl: Anal ys i sc)

ln G;ofp=

covariance forBG/(BG + G); d)

a) 'ln BG; b)I nIp/ ( t-p)] .

Mean

I(i)J

I

a)

b)

c)

Source

R. F.I.A.S.A.B.

Res i dual

R. F.I.A.s. A.B.

Resi dual

R. r.I.A.S. A.B.

Res i dua I

R. F.I.A.S.A.B.

Res i dual

Sum ofares

7r2.35140.53

7 .7579.00

444.30

242.3341 .159.927 .59

300.24

4.4t4.49

.13

.839.86

707 .9434.118.58

14 -41139.59

Degrees ofFreedom are

772.3523.421.29

TT.292.27

242.336.861 .65i .081 .53

4.41.75.02.12.05

707 .945.691 .432.06

.77

TestStati stí c

374.2*10.33*

1

5 .0*

1 58 .4*4.5*1

1

88.2*15.0*I2.4*

997.l"*9.0*2.02.9*

1

667

196

I667

196

1

667

196

1

667

196

R2

.51

.62

.62

.68

.40

.47

.49

.49

.2?

.45

.46

.50

.78

.82

.83

.85

.51

.i1

.00

.06

.40

.07

.02

.01

.22

.23

.01

.04

.78

.04

.01

.02d)

R. F. : Reference LakeI,A.: Intercept adjustment for individual test lakesS.A.: Slope adjustment for individual test lakesB. : Pre/Post ban adjustment for intercept

*Statístically significant at at least 5% level.

TABLE G2:

Swan

Bal sam

Elk

.64

.74

3 .08* .33* .37*

.15 .98*

.19 .70*

.29 .84*

1,.47* .70*

0 ..94*

.2r . 86*

-.25 'l .ì1*

Estimates of pre/post ban effect on íntercept andcorresponding reference lake for ln BG, 1n Go p

tpl(l-p)1.

slope(s) for= BG/(ee + G), and ln

p 1n Ip/(l-p)]ln Gïn BG

Lake Intercept S'l ope Intercept S'l ope Intercept Sl ope Intercept Sl ope

Butternut 1.61*

.83*

.65*

. B1*

.62*

1 .06*

.26

.34

.47

.91

.18

.52

.90

1.03*

.67

.85*

.7r*

.57

.50

.51

.07

.04

.09

.44*

.48*

.60*

?o*

.61*

Enterprise -.91 .05

.07Ic,N)I

Moss

Townl i ne -1.23

Approxi -mate stand-ard devi-at'i on . B0

- .58 1.06

.98* -.11 .54*

.09.35.90.17 .09.34.13

*Statistically significantly different from 0 at at ìeast the 5% ievel

APPENDIX H

Vol lenwe'ider Loading Criter'ia

APPTNDIX H

Vol lenweider Loadi ng_ Criteria

The phosphorus model based on mean depth and hydraulic resjdence time,

developed by Vollenweider (1975), was used as a quant'itative guideline by which to

judge the magnitude of the effect of phosphate detergents on the test lakes. This

model compares the actual areal loading of phosphorus (g p/m2 lake surface/yr) to

permissible and critical loading rates calculated from the model. The formula used

for determ'ining the critical loading rate was:

L. = 0.02

where L. = critical loadíng rate for phosphorus

(g/^2 /yr)I = mean depth of 'lake (m)

= hydraulic residence time of lake (yr)

V, = sedimentat'ion vel oc'ity (m/yr)

For these'lakes, the value of 10 m/yr for V, was used (Vol'lenweider, 19i5). The

permissible criterion js one-half the crjtical loading criterion.

-H1-