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SDMS Document
110765
INTERIM CLEANUP LEVELS INTERIM REPORT #2
RISK ASSESSMENT REYNOLDS METAL COMPANY
Prepared for
U.S. ENVIRONMENTAL PROTECTION AGENCY Emergency and Remedial Response Division
26 Federal Plaza New York, New York 10278
Work Assignment No.:
EPA Region:
EPA Site/Facility I.D. No.:
Contract No.:
Document No.:
Alliance Project No.:
Alliance Project Manager:
Telephone No.:
Subcontractor No.:
Subcontractor Project Manager:
Telephone No.:
EPA Work Assignment Manager:
Telephone No.:
Date Prepared:
C02082
n NYD002245964
68-W9-0003 (TES 6)
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1-635-236-0-2P4D
Naida Gavrelis
(508) 970-5600
N/A
N/A
N/A
Lisa Carson
(212) 264-6857
September 4, 1991
ATTTANCE TECHNOLOGIES CORPORATION 291 Broadway, Suite 1206
New York, NY 10007 / m i x 1Al\ ACMi
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TABLE OF CONTENTS
Section Page
1.0 INTRODUCTION 3
2.0 BACKGROUND 3
3.0 METHODOLOGY FOR ESTABUSHING CLEANUP LEVELS 4
4.0 RESULTS 7
5.0 DISCUSSION 13
6.0 COMPARISON WITH OTHER PCB CRITERIA . 16
REFERENCES 18
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1.0 INTRODUCTION
Alliance Technologies Corporation (Alliance) imder Work Assignment C02082 of
EPA Contract 68-W9-0003 (TES 6) was requested to derive human health risk-
based interim cleanup levels for PCB-contaminated sediments in the St. Lawrence
River adjacent to the Reynolds Metal Company (Reynolds) site in Massena, New
York. The method to derive risk based cleanup levels, the values derived, and
the uncertainties used are described below.
2.0 BACKGROUND
Target cleanup levels (preliminary remediation goals) are established to provide
levels of contaminants of concern in affected media that will be protective of
human health and the environment. They are calculated using the mediimi-
specific target risk range of 10" and 10"* established by the National Contingency
Plan. At the Reynolds site, PCBs (polychlorinated biphenyls) in sediments are the
contaminants of primary concern. PCBs were routinely used by Reynolds in their
production process and have been detected in sediments in the St. Lawrence
River adjacent to the Reynolds site at concentrations ranging from not detected
(ND) to 550,000 Mg/kg. Area residents may be exposed to sediments directly by
dermal contact or incidental ingestion. However, the greatest potential risk
resulting from human exposure to PCBs in the vicinity of the Reynolds site is
likely to be via the ingestion of PCB-contaminated fish. Total PCB concentrations
ranging from ND to 81,490 /ig/kg have been detected in fish collected in the St.
Lawrence and Raquette Rivers.
Two general groups, the Mohawk native population and recreational fishermen,
fish in the vicinity of the Reynolds site. The Mohawk Nation reservation is o
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located on the St. Lawrence River 0.7 miles north of Reynolds on Cornwall Island
and 1.1 miles downstream at Raquette Point. Locally caught fish comprise a large
portion of the nearby Mohawk Nation population's diet Preferred species
include: northern pike, yellow perch, small mouth bass, bullhead, catfish,
sturgeon, and walleye pike (Jock, 1991). Recreational fishing in the lower reaches
of the St. Lawrence River (where Reynolds is located) is dominated by local
residents; 63 percent of the anglers in 1982 were from St. Lawrence County
(McCuUough, 1987). Canadian anglers were the largest group of non-New York
State anglers (comprising 10%) in this area of the St. Lawrence (McCullough,
1987). The preferred fish species among recreational anglers in both 1982 (in
American waters) and 1985 (in Canadian waters) were reported as: yellow perch,
northern pike and small mouth bass. Other preferred species included large
mouth bass and rock bass (McCullough, 1987 and Hart, 1986). The target
cleanup level analysis focused on fish species preferred by the Mohawk Nation
population because of its heavy consujnption of locally-caught fish. These fish
species are also the preferred species of recreational anglers.
3.0 METHODOLOGY FOR ESTABLISHING CLEANUP LEVELS
Data on PCB concentrations in fish tissue were obtained firom a study conducted
by the New York State Department of Environmental Conservation (NYSDEC)
and the St. Regis Mohawk Tribe Environmental Programs (Sloan and Jock, 1990).
These data were collected as part of a health risk assessment for the nearby GM
Foundry site. Data on PCB concentrations in sediments were obtained from the
Additional River Sampling Report (Woodward-ayde, 1991). This report presents
^ the findings of the investigation of the extent of contamination in the sediment
and surface water in the St. Lawrence and Raquette Rivers in the vicinity of the
o Reynolds site.
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Fish and sediment samples were analyzed for several different Aroclor mixtures.
PCB concentrations in fish were reported by NYSDEC as Aroclor 1221, 1016, and
1254, but Ukely include other Aroclor such as 1248 and 1260. PCB concentrations
in sediment were reported as Aroclor 1016, 1221, 1232, 1242, 1248, 1254, and
1260. Reported mixture-specific PCB concentrations were summed to produce
separate total PCB values for fish and sediment, which were used throughout this
analysis. The technique of summing reported PCB values should result in
comparable total PCB concentrations, exclusive of differences in the mixtures
reported by laboratory analysis.
In order to derive a risk-based sediment cleanup level it was first necessary to
estimate the PCB concentration in fish tissue which would produce a carcinogenic
risk within the NCP target range (10^ to 10"*). Consistent with EPA risk
assessment guidance (1989 and 1991) and available site-specific information, the
following equation and exposure peirameters were used to back-calculate from
target risk levels to PCB concentration in fish:
(1) PCB Concentration = Risk x BW x AT x CF in Fish Tissue (/ig/kg) CSF x IR x H x EF x ED
where: BW = Body weight = 70 kg AT = Averaging time = 25550 days CF = Conversion factor = 1 x lO' Mg/nig CSF = Cancer slope factor for PCBs = 7.7 (mg/kg/day)-^ IR = Ingestion rate = 0.132 kg/day FI = Fraction ingested from contaminated source =
1 (unitless) EF = Exposure frequency = 350 days/yr ED = Ejqwsure duration = 70 years
In order to relate these PCB concentrations in fish tissue to concentrations in
sediment, it was necessary to derive sediment-based bioaccumulation factors (fish
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to sediment concentration ratios). Bioaccumulation factors (BAFs) were derived
using the following equation:
(2) BAF = £f
A Reynolds site-specific BAF was calculated using:
(a) Cf = The maximimi total PCB concentration in fish (carp) caught
immediately adjacent to Reynolds site outfalls, and
Cj = Arithmetic mean total PCB concentration in area 3B (area adjacent
to Reynolds site outfall)
In an effort to provide a context for the above BAF and utilize a larger data set,
two area-wide BAFs were also calculated using:
(b) Cf = Arithmetic mean total PCB concentration in aU preferred fish species caught throughout the St. Lawrence River System, and
Cj = Arithmetic mean total PCB concentration in all sediment samples collected near the Reynolds site.
and
(c) Cf = Maximum total PCB concentration in preferred fish species, excluding fish caught in the area in front of GM (another source of PCBs along the St. Lawrence River). The maximum PCB concentration was reported in channel catfish caught at the mouth of the Grass River, approximately 0.9 mile upstream of Reynolds.
Cj = Arithmetic mean total PCB concentration in ail sediment samples collected near the Reynolds site.
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The rationale for these three BAF scenarios is presented in the discussion section
below (Section 5.0).
Sediment cleanup levels were derived based on calculated BAFs using the
following equation:
(3)
where
Cf
BAF =
Q = £f BAF
concentration of PCBs in sediment producing an increased carcinogenic risk of 10" and 10"* to hmnans based on consumption of fish which may have fed in areas with contaminated sediment
concentration of PCBs in fish tissue producing an increased carcinogenic risk of 10"* and 10"* to humans consuming fish.
Bioaccumulation factor as previously described.
4.0 RESULTS
Table 1 presents the spreadsheet used to calculate PCB concentrations in fish
tissue that would result in a 10^ and 10"* carcinogenic risk.
Mean total PCB concentrations calculated for fish and sediments are presented in
Table 2. Calculated mean PCB concentrations in fish tissue range from 1,780 to
46,845 Mg/kg. Calculated mean PCB concentrations in sediment were 93,184 and
184,418 /ig/kg.
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The calculated BAFs (Table 3) range from 0.02, when PCB concentrations in
preferred fish species and aU sediments are used, to 0.5, when the maximtmi PCB ^ -<
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concentration in fish and all sediments are used. When fish and sediment near
Reynolds are used, the BAF is 03.
At the 10"* risk level, sediment cleanup levels (Table 4) range from 0.2 MgA&
using maximum PCB concentration in fish and all data for PCB concentration in
sediment, to 4 jug/kg, using PCB concentration in all preferred species and all
data for PCB concentration in sediments. When PCB concentrations in carp and
sediments collected near Reynolds are used to calculate BAFs, calculated
sediment cleanup levels are 03. At the 10^ risk level, these cleanup levels
increase to 20, 400, and 30 Mg/kg, respectively.
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TABLE 1. PCB CONCENTRATIONS IN FISH TISSUE BACK-CALCULATED FROM INCREASED CANCER RISKS.
Exposure Scenario
Local Resident
Contaminant of Concern
PCBs
Increrased Cancer
FBsk
1.00E-06
1.00E-04
Concentratton ihRsh {ugfl«g}
0.072
7.182
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TABLE 2. MEAN PCB CONCENTRATIONS IN FISH AND SEDIMENTS NEAR REYNOLDS
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RSHr Maximum PCB Concentrations in Carp Caught in Area 3B (Upstream of Reynolds);
AR-1248 AR-1254
, AR-1260
TOTAL
Mean PCB Concentrations in Preferred Species:
AR-1016 AR-1221 AR-1254
TOTAL
liiiliiiiiiiilii _ . ^ . , „ . - . . . . . . . . • _
19000.00 ug/kg 25000.00 ug/kg
4400.00 ug/kg
48400.00 ug/kg
573.096 ug/kg 30.88 ug/kg
1176.10 ug/kg
1780.07 ug/kg
Maximum PCB Concentrations in Channel Catfish Caught Near the Mouth of the Grass River (Upstream of Reynolds):
AR-1016 AR-1221 AR-1254
TOTAL SEDIMENTS:.
Mean PCB Concentrations in Sediments from Area 3B:
AR-1242 AR-1221 AR-1016 AR-1248 AR-1254 AR-1260
TOTAL
Mean PCB Concentrations in Sediments from All Areas:
AR-1260 AR-1248 AR-1242 Afl-1232 AR-1254 AR-1221 AR-1016
TOTAL
2030.00 ug/kg 25.00 ug/kg
44790.00 ug/kg
46845.00 ug/kg
iBiliiiiiiiiiiii
48916.23 ug/kg 19685.00 ug/kg 19280.79 ug/kg 19532.37 ug/kg 38551.05 ug/kg 38452.28 ug/kg
184417.72 ug/kg
19549.63 ug/kg 9960.69 ug/kg
24148.89 ug/kg 70.00 ug/kg
19606.50 ug/kg 10033.77 ug/kg 9814.59 ug/kg
93184.07 ug/kg
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TABLE 3. BIOACCUMULATION FACTOR CALCULATIONS
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RshType
Carp from Area 3B:
Preferred Species:
Channel Catfish:
PCB Cone. (Cf}
(ugflcg>* 48400.00
1780.07
46840.00
Sediment Area
Area 3B:
All Areas:
All Areas:
PCB Cone. <Cs>
184417.72
93184.07
93184.07
| | | | | | B | | | | | i | :
0.019
0.503
see Table 2.
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TABLE 4. SEDIMENT CLEAN-UP LEVELS
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Sediment Clean-Up Levels for Area 38 Based on Carp BAF in Area 3B: increased
Cancer Risk
1.OOE-06
1.00E-04 •
; Backcalculated BAF** Fish Cone,
(ugflcg)-0.084 0.262
8.379 0.262
i Sediment Clean-Up
Level (ug/kg) 0.3
30 Sediment Clean-Up Levels for All Areas Based on Preferred Species BAF in All Areas:
Increased Cancer
Risk
1 .OOE-06
1.00E-04
Backcafculated BAF-* Rsh Cone,
(ug/kg)-0.084 0.019
8.379 0.019
Sediment Cfean-Up
Level (ug/kg) 4
400 Sediment Clean-Up Levels for All Areas Based on Channel Catfish BAF in All Areas:
Increased 1 Cancer
Risk 1.OOE-06
1.00E-04
Backcalculated BAF** Rsh Cone,
(ugfl^g)* 0.084 0.503
8.379 0.503
Sediment Clean-Up
Level (ug/kg)
0.1
10
9 * see Table 1. * * see Table 3.
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5.0 DISCUSSION
Site-specific BAFs were estimated using available data on PCB concentrations in
both fish and sediment collected near the Reynolds site. Models exist that
estimate contaminant concentrations in the water colmnn based on concentrations
in sediment or that estimate contaminant concentrations in fish based on
concentrations in the water column (e.g., EXAMS/WASP4, and SGETS).
However, for this analysis a site-specific BAF was calculated because it is believed
that this method would produce a more realistic site-specific estimate of PCBs in
sediments. This decision was made based on consultation with the EPA WAM
and an evaluation of the benefits and limitations of existing models.
Since the BAFs derived for the purpose of calculating cleanup levels are the
driving force in the final calculation, a more detailed discussion on the rationale
behind the selection of the equation parameters is warranted. Equation 2a uses
the maximum total PCB concentration measured in carp caught immediately
adjacent to Reynolds and sediments in area 3b (the Reynolds outfall) to calculate
a Reynolds-specific BAF. The maximvun total PCB concentration was used
because of the limited number (two) of samples available. While carp is not a
preferred species for local consumption, it may provide a conservative
approximation of PCB concentrations in preferred fish species exposed to PCB-
contaminated sediments resulting from the Reynolds site. Carp have a limited
home range (Sloan and Jock, 1990). Therefore, carp collected adjacent to
Reynolds outfalls are likely to have been exposed to contaminants arising fi-om
these outfalls, although they are unlikely to have fed exclusively on these
sediments. Carp also have a relatively high fat content and since there is a
positive association between fat content and PCB concentration (Sloan and Jock,
1990), PCB concentrations in carp may be at the high end of the range found in
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all fish. However, whether the PCB concentrations found in the carp sampled are
representative of PCB concentrations foimd in all fish exposed to Reynolds- -
contaminated sediments is imcertain because of the small number (n = 2) of fish
sampled. Small samples do not necessarily provide an accurate estimate of
patterns in the entire population, j - r ; - - : ,5 - :: . n:; ::\.uy.
Two area wide BAFs were calculated in an effort to provide a context for the
Reynolds-specific BAF calculated. The first set of area wide Cj and C values
(Equation 2b) was used to approximate an average BAF for commonly consumed
fish species in the St. Lawrence River System that could have potentially
consumed sediments contaminated by PCBs from Reynolds. Selecting only
preferred fish species reflects likely exposure to local populations. Fish collected
at all locations were included here because fish are mobile and even those caught
8 miles upstream or downstream fi-om the Reynolds site could have consxmaed
site-related contaminants via sediments or biota. The mean total PCB
concentration for preferred fish species was used to represent a river-wide average
condition. While it is recognized that fish vary in typical mobility patterns (Sloan
and Jock, 1990), mobility patterns for a given fish species can change with season
and habitat (Sloan, 1991); Therefore elimination of data from fish typically having
a "restricted home range" seemed unwarranted, especially when balanced against
the disadvantage of decreasing already small sample sizes. Likewise, use of data
for all available sediment samples collected near the Reynolds site fi-om WCC
(1991), rather than those for only highly contaminated sediments was assumed to
better represent the conditions to which fish in the St. Lawrence River System are
actually exposed.
rn I The second set of area wide Cf and C values (Equation 2c) was used to calculate
a BAF based on the highest level of contamination (total PCBs) reported for fish o o
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tiiat could have potentially consumed sediments contaminated by PCBs from the
Reynolds site and that were collected outside the immediate vicinity of the GM
plant. A maximmn was selected to represent a potential worst case. Once again,
all available sediment data from WCC (1991) were used in deriving Cj.
The cleanup levels presented in this report are, of necessity, based on limited data
sets and a number of underlying assimiptions regarding these data. While PCB
concentrations in carp and sediment collected adjacent to the Reynolds site
represent the most site-specific data available, uncertainty in the cleanup level
estimate results from: (1) the small number of carp sampled; (2) the possibility
that fish collected near Reynolds are feeding on sediments (and biota) from a
variety of areas within the St. Lawrence River System, including uncontaminated
areas and areas contaminated with PCBs from other sources (e.g., GM and
Alcoa); (3) the unknown relative contribution of the Reynolds site to PCBs
throughout the area of the St. Lawrence River System from which fish were
collected; (4) the possibility that the relative concentrations of PCBs in fish and
sediment have changed over time, as fish and sediment samples were not
collected concurrentiy; and (5) the possibility that contaminant concentrations in
carp do not accurately reflect contaminant concentrations in commonly consimaed
fish species due to differences among species in lipid content, mobility, and
feeding habits.
Many of the same limitations apply to data used to calculate cleanup levels based
on area-wide BAFs. Contaminant concentrations in sediments are highly
heterogeneous within the home range of any given fish species. This
heterogeneity limits direct linkage between contaminant concentrations in
sediments in a given area and contaminant concentration in fish tissues. Caging
fish and their prey in an area of known sediment contaminant concentrations may 73
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be the one way to obtain direct correspondence between these two data types. A
further consideration is the trophic level of the fish involved. Since PCB
concentrations would tend to increase in fish at higher trophic levels, the trophic
level of the species used as a model is likely to impact the BAFs calculated.
6.0 COMPARISON WITH OTHER PCB CRITERIA
As a basis of comparison, interim sediment criteria developed by U.S. EPA and
New York State are presented below . The U.S. EPA (1988) has developed an
interim sediment criterion for PCBs based on Aroclor 1242. Since the capacity
for sediments to retain PCBs increases with increasing organic carbon content of
the sediment, the sediment criteria are calculated based on the organic carbon
content of the sediment. The 95% confidence interval of criteria designed to be
protective for the consumption of aquatic biota ranges from 38.7 to 999 Mg/kg
(with a mean of 195 Mg/kg) for sediment with an organic carbon content of 1%
and 387 to 9990 Mg/kg (with a mean of 1950 Mg/kg) for sediment with an organic
carbon content of 10%. Sediments in the SL Lawrence River are likely to have
an organic carbon content between 0 and 10 percent based on experience at other
sites and professional judgment. Confidence intervals are given to emphasize the
uncertainty in the calculation of these values. This criterion was calculated using
the equilibrium-partitioning approach and a Food and Drug Administration
(FDA) action level of 5000 Mg/kg. Since its development, the FDA action level
has been lowered to 2000 Mg/kg. Furthermore, bioaccumulation within the food
chain is not accounted for in the calculation of BAFs used in the development of
this criterion. It is estimated that bioaccumulation in the food chain may result in
— BAFs ten times greater than laboratory measured BAFs (EPA 1988). Also,
^ different PCB congeners vary in their toxicity, accumulation, and metabolism, -<
adding additional imcertainty to these values (EPA 1990).
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New York State has developed ±eir own guidance sediment criteria (NYSDEC,
1989), using both an equilibrium-partitioning approach and a bioaccumulation
approach. When an equilibrium-partitioning approach was used (based on a
proposed ambient water quality standard of 6 x 10^ Mg/1), tiie sediment criteria
assuming 1% organic carbon is 0.08 Mg/kg and assuming 3% organic carbon is
0.24 Mg/kg. This criterion is based on a lO"* cancer risk from fish consiunption.
The NYS criterion is lower than the EPA value derived by the same method
because:. (1) the water quality criterion used by EPA was derived from a BAF
lower than beUeved to be reaUstic by NYS, and (2) the fish flesh criterion used by
EPA for wildlife is lower than beUeved prudent by NYS (NYS 1989). NYS used
a second approach, the bioaccumulation approach, to calculate a criterion for
PCBs. Using this approach and assuming an edible fillet with 3% lipid and
sediment with 3% organic carbon, the sediment criterion range calculated for
PCBs is 0.6 to 0.06 Mg/kg. These values were calculated assuming a 10" cancer
risk, 0.5 pound per week fish consumption, and sediment to fish accumulation
factors ranging from 1 to 10.
The sediment cleanup values presented in this report fall within the range of
criteria developed by the U.S. EPA and NYS; however this is a very broad range
spanning five orders of magnitude, depending on the method used and initial
assumptions.
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REFERENCES
Hart, M.L. 1986. St. Lawrence River Summer Creel Census, 1986. Ontario Ministry of Natural Resources.
Jock, K, 1991. St. Regis Mohawk Tribe Environmental Programs. Personal communication with Naida Gavrehs, Alliance Technologies Corporation.
McCullough, R.D. 1987. The Summer Boat Fishery of the St. Lawrence River, 1982. NYS DEC, 1987 St. Lawrence River Subconunittee Report, Great Lakes Fishery Commission.
NYSDEC. 1989. Sediment Criteria. Bureau of Environmental Protection, Division of Fish and Wildlife.
Sloan, RJ. 1991. NYS Department of Environmental Conservation. Personal communication with Dolores Savignano, Alliance Technologies Corporation.
Sloan, R J . and K. Jock. 1990. Chemical Contaminants in Fish from the St. Lawrence River Drainage on Lands of the Mohawk Nation at Akwesasne and Near the General Motors Corporation Central Foundry Division Massena, New York Plant. NYSDEC Technical Report 90-1 (BEP) Division of Fish and Wildlife, 96 pp.
U.S. EPA, 1989. Risk Assessment Guidance for Superfund, Volume I and IL Office of Emergency and Remedial Response.
U.S. EPA, 1991. Risk Assessment Guidance for Superfund, Volume I, Supplemental Guidance: Standard Default Exposure Factors, Interim Final Office of Emergency and Remedial Response.
U.S. EPA- 1990. Guidance on Remedial Actions for Superfund Sites with PCB Contamination. Office of Emergency and Remedial Response, EPA/540/G-90/007.
U.S. EPA. 1988. Interim Sediment Criteria Values for Nonpolar Hydrophobic Organic Contaminants. Office of Water Regulations and Standards, Criteria and Standards Division.
Woodward-Clyde Consultants. 1991. Draft Additional River Sampling Report: St. Lawrence River System, prepared for Reynold Metals Company, Massena, NY.
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