BIRD IN HAND GOLD PROJECT - Terramin Australia Limited · sampled in 2017. The current report...

BIRD IN HAND GOLD PROJECT MINING LEASE PROPOSAL MC 4473

ABN | 66 122 765 708 Unit 7 / 202-208 Glen Osmond Road | Fullarton SA 5063

APPENDIX Q4

2018 STYGOFAUNA STUDY

Bird In Hand Stygofauna Investigation

8 June 2018

Terramin Exploration Proprietary Limited

Bird In Hand Stygofauna - Terramin 2

Document Control

Report Number Status Date Author Reviewer

BIH‐ENV‐2018Fauna01-V1 Draft 13/2/2018 Alistair Cameron Matt Daniel

BIH‐ENV‐2018Fauna01-V2 Final 8/6/2018 Alistair Cameron Matt Daniel

Inquiries on this report can be made to:

Matt Daniel | Environment & Community Superintendent Terramin Exploration Pty LtdUnit 7, 202-208, Glen Osmond Road, Fullarton, SA 5063, Australia T : 08 82131415E: [email protected]

Please refer to this document as:

Terramin, Bird In Hand Stygofauna, Report # BIH‐ENV‐2018Fauna01-V2. 2018.

Table of Contents

1. INTRODUCTION ................................................................................................................................................ 5

mailto:[email protected]


1.1 STYGOFAUNA AND SUBSURFACE GROUNDWATER DEPENDENT ECOSYSTEMS ..................................................................... 5 1.2 DISTRIBUTION OF STYGOFAUNA IN SOUTH AUSTRALIA .................................................................................... 7 1.3 SA GROUNDWATER POLICY AND LEGISLATION ................................................................................................. 8 1.4 GEOLOGY AND GROUNDWATER ........................................................................................................................ 8 1.5 PROJECT OBJECTIVES ............................................................................................................................................. 9

2. METHODOLOGY ............................................................................................................................................. 10

2.1 SAMPLING SITES .............................................................................................................................................. 10 2.2 SAMPLING METHODOLOGY .................................................................................................................................... 10

3. RESULTS ............................................................................................................................................................ 13

4. DISCUSSION AND CONCLUSION ................................................................................................................ 16

5. REFERENCES ................................................................................................................................................... 18

6. APPENDICES ..................................................................................................................................................... 19

List of Tables

Table 1 Groundwater conditions favourable for stygofauna and aquifer conditions at BiH. ....................... 8

Table 2 Sample site and date ...................................................................................................................... 10

Table 3 Physical attributes and type of aquifer at the groundwater bores sampled ................................. 13

Table 4 Water Quality attributes of ground water bores at time of sampling 2014 and 2015. .................... 14

Table 5 Water Quality attributes of ground water bores at time of sampling 2017. ................................... 14

Table 6 Stygofauna sample results. ............................................................................................................. 15

List of Figures

Figure 1 Bird in Hand Location, showing historic mine workings ............................................................... 6

Figure 2 Bore locations. .............................................................................................................................. 11

Figure 3 Conceptual design of pump test bores .......................................................................................... 12

Abbreviations

BiH Bird in Hand

SGDE Subsurface groundwater dependent ecosystems

DO dissolved oxygen

EC electrical conductivity

TDS total dissolved solids


Executive Summary

This report follows on from the previous stygofauna conducted by Terramin (2016) and the

recommendation by COOE (2014) for a two-stage baseline stygofauna sampling survey in conjunction with

groundwater quality sampling. COOE (2014) had identified groundwater dependent ecosystems and the

possible presence of stygofauna as potential management risk in the operation of Bird-In-Hand (BiH) Mine.

3 bores were examined in 2014 and 4 bores in 2015. This report presents the data from a further 5 bores

sampled in 2017. The current report contains the all data presented in Terramin (2016) and therefore

supersedes the previous report.

The projects objectives were to confirm the presence or absence of Stygofauna in samples taken in bores

near the proposed underground mine; provide a report on search effort, GW water quality for sample,

geological unit; and provide items of interest and proposed distance to underground operations.

Water quality data collected during the survey indicated wide varying results within and between sites

during the sampling process. pH was most acidic at 6628-8301 although the most acidic reading was

recorded from 6628-8945. Dissolved Oxygen readings varied greatly and it is suggested that the sampling

methodology would have influenced the recordings through artificial aeration. TDS were similar at all sites

but with 6628-8301 appearing considerably higher than all other sites. Electrical Conductivity was also the

highest at 6628-8301. 231086 was the only site to exhibit readings that were consistently below the

previously reported favourable threshold of 1.5 mS/cm. High ions were recorded at 6628-8301, which is

indicative of the high EC recorded from the site. Na+ and Cl- dominated the ion concentration. High levels

of Manganese were recorded at 231090, 231086 and 6628-8301. A high concentration of Total N was

recorded at 231087 with 1.0 mg/L, 6628-27447 with 1.4 mg/L and at 6628-8301 with 3.4 mg/L. All other

readings were below drinking water trigger values.

Examination of the stygofauna samples indicated no stygofauna were present in any of the samples. While

some fauna were identified they were all of terrestrial origin. Depth of the bores and high salinity appear

to be outside the known habitat preferences. Additionally the historical and recent groundwater

abstraction for irrigation and consumption purposes, identified the lack of stygofauna food items, and the

presence of clay aquitards (Golders 2017) within the area together could be possible explanations of a lack

of Stygofauna. The groundwater abstraction seasonally lowers the water table reducing habitat value, and

potentially removing Stygofauna. The aquitards and low permeability rock zones, outside of groundwater

bearing fractures, identified in the above mentioned Terramin groundwater study would also prevent or

slow migration of stygofauna back to an area where they might have become locally extinct.

In conclusion, the samples examined indicated that stygofauna are not present in the BiH study area and

that current water quality and structure of the groundwater bearing fractures would prevent their

presence.


1. INTRODUCTION

This report follows on from the previous stygofauna conducted by Terramin (2016) and the

recommendation by COOE (2014) for a two-stage baseline stygofauna sampling survey in conjunction with

groundwater quality sampling. COOE (2014) had identified groundwater dependent ecosystems and the

possible presence of stygofauna as potential management risk in the operation of Bird-In-Hand (BiH) Mine.

3 bores were examined in 2014 and 4 bores in 2015. This report presents the data from a further 5 bores

sampled in 2017. The current report contains the all data presented in Terramin (2016) and therefore

supersedes the previous report.

Terramin (2016) provides the site history of the Bird-In-Hand (BiH) Mine site that is located within the

Western Mount Lofty Ranges three kilometers east of the Adelaide Hills township of Woodside, and 25 km

east of Adelaide, South Australia (Figure 1). Fradd and Morris (2015) also provide an extensive summary

of the history of the BiH mine as well other mines in the larger Woodside area. As previously reported in

Terramin (2016) BiH mine was established in 1882 but closed in 1889 due to financial and water

management difficulties. Between 1915 and 1916 treatment of tailings yielded 846.4 grams of gold

bullion. Between 1932 and 1934 the mine was dewatered and explored by the South Australian Mines

Department. From 1934 to 1967 groundwater has been extracted as supply for Inverbrackie Barracks.

Ownership of the mine transferred to from the Commonwealth to State government in the 1960’s and the

site was primarily used for storing fill materials that included, concrete, building materials and asphalt.

Maximus Resources explored the area between 2005 and 2013 with diamond and percussion drilling and

released an indicated and inferred resource of 598 000 tonne at 12.3 g/t Au for a contained 7371.5 kg (237

000 oz) gold to 430 m vertical depth at a depth which is about 325 m deeper than the original mine

workings. Terramin then acquired the Mineral Claim in July 2013 and a nearby farming property July 2015,

exploration has been ongoing, informing the forthcoming Mining Lease Application.

1.1 Stygofauna and Subsurface Groundwater Dependent Ecosystems

As previously identified by Terramin (2016) Subsurface Groundwater Dependent Ecosystems (SGDEs)

include ecosystems that are below the surface that would be significantly altered through the changes in

the water quality of groundwater, changes to water levels or removal of groundwater, and compaction of

sediment.

SGDEs include stygofauna and troglofauna, as well as terrestrial vegetation and wetland communities that

are sustained by the groundwater. Troglofauna are air-breathing organisms living in subterranean cavities

such as caves or small air filled voids and this type of habitat is absent from the study area. Troglofauna

include arachnids, millipedes, beetles, crickets, cockroaches and many other invertebrate species.

Troglofauna are not considered further in this reporting. Additionally, types of groundwater dependent

ecosystems, which rely on the surface expression of groundwater to sustain terrestrial and riparian plants,

wetlands or stream base-flows are not examined in this report. Finally, terrestrial or flying organisms that

fall into boreholes may also be sampled in groundwater.

Stygofauna generally consist of predominately crustaceans, as well as worms, snails, insects and a few


other invertebrate groups. Fish have also been described (rarely) as stygofauna, such as the Blind Gudgeon

and Blind Cave Eel of Western Australia. They are found in aquifers that may be associated with existing

features of the land surface such as permanent, seasonal or ephemeral watercourses. Stygofauna have

been characterised into three broad groups: stygoxenes, that are surface-dwelling species that are

occasionally transported to groundwaters; stygophiles, that are widely found species that use both

groundwater and surface waters as part of their life cycles; and stygobites, which are obligate dwellers in

subterranean waters. The latter group typically displays common morphological characteristics, such as

loss of eyes, pale or no pigmentation and enhanced sensory structures (Eberhard 2007). Given the isolation

of many aquifers, stygofauna may exhibit high levels of endemism (i.e. species that are restricted to

particular localities). DNA analyses are required to discriminate taxonomic groups where identification of

species based on morphological features is not currently reliable.

Figure 1 Bird in Hand Location, showing historic mine workings

SGDEs differ from surface ecosystems in both the types of biota present and the major driving processes.

In contrast to surface water ecosystems, groundwater ecosystems are usually considered to have relatively

stable conditions and physically inert environments. However, many groundwater ecosystems undergo

substantial changes through space and time, related to fluxes in groundwater flow, exchange and nutrient

imports (Mencio et al. 2014). Additionally, the absence of light means that there are usually no primary

producers (e.g. higher plants and algae) driving the food webs of subsurface groundwater ecosystems,

although a small amount of primary production can occur through chemo-autotrophic bacteria and

protozoa that derive their energy through chemical reactions with inorganic molecules such as hydrogen

sulfide, elemental sulfur and ammonia under an anaerobic or low oxygen environment (Hose and Lategan


2012). The ecosystem is often dependent on the processing of carbon filtering down from the surface and

metabolised by bacteria and fungi at the base of the aquifer food web (Boulton 2000). A simplified food

web in a SGDE would be the microbes in these aquifers forming biofilms that are grazed by protozoa and

the meiofauna (i.e. fauna between 1 mm mesh and 45 μm), such as rotifers and nematodes, which in turn

are grazed by macro-invertebrates.

Although are studies on Australian stygofauna are in their youth, it has been that shown that there is a

wide variety of subterranean species and Australian SGDEs are gaining international renown (Goonan et

al. 2015). At least 750 Australian stygofauna species have been found so far, which represents about 22%

of the global total and highlights Australia as a groundwater biodiversity hot zone (Humphreys 2008). Most

groundwater ecosystem studies have been focused in Western Australia, particularly from areas such as

the Pilbara and Yilgarn that are undergoing large-scale exploration and mining developments. However,

surveys in recent years have also shown significant biological richness in alluvial, fractured rock, karstic

and calcrete aquifers across the Northern Territory, New South Wales, Queensland and Tasmania

(Tomlinson and Boulton 2008). In Australia, many stygofaunas in arid areas occur in brackish to saline

waters, although they contain taxa from lineages generally restricted to freshwater systems (Humphreys

2006).

Threats to stygofauna have been identified as disturbance of groundwater habitats, such as water

extraction, artificial filling and contamination (including introduction of toxic chemicals or clogging of pore

spaces by fine sediments) (Tomlinson and Boulton 2010, Humphreys 2006). Their low dispersal capabilities

and fecundity makes them susceptible to habitat disturbances and at risk of extinction. Life-history

adaptations of stygofauna to the groundwater environment, such as production of fewer but larger eggs,

prolonged egg development and greater longevity compared with surface-dwelling relatives, may make

them more susceptible to environmental disturbance (Tomlinson and Boulton 2010).

1.2 Distribution of stygofauna in South Australia

In 2007 the Australian Research Council initiated a study with the aim of describing stygofaunal and

microbial diversity in South Australian aquifers (Goonan et al. 2015). Since that time, the project has

sampled 547 sites, with approximately half the sites containing stygofauna. The survey conducted between

2008 and 2010 by the Flinders University (Leijs unpublished, Leijs 2008, Leijs 2010 sited by COOE 2014)

resulted in the discovery of more than 100 new species. This taxonomic diversity ranged across a number

of different invertebrate groups from all aquifer types in various parts of South Australia (South East,

Mount Lofty Ranges, Flinders Ranges, York Peninsula and Eyre Peninsula).

Although the Lofty Ranges area was not systematically surveyed, stygofauna were found in most spring

habitats sampled. Species diversity was high and the majority of the species were only found at single

localities (COOE 2014). A new species of Neoniphargid amphipod was found in a spring at Spring Creek

near Burra Gorge, as well as a Bathynellid species in a groundwater observation bore north of Burra. The

significance of these finds was suggested as increasing the expectation of occurrence of stygofauna

elsewhere in the Mount Lofty Ranges (Leijs 2008, 2009).


Stygofauna sampling localities closest to the BiH project area are: Piccadilly Springs, springs on private

properties near Crafers and along Brown Hill Creek, and a hyporheic site in Cox Creek near Mylor. All these

localities had assemblages of fauna with unique species, which are likely associated with fractured rock

aquifers.

In 2016 the examination of the bores 231087, 231090, 231089, ONK 20, 6628-8945, 231086 and 6628-

8301 indicated the absence of stygofauna. The bores examined had elevated electrical conductivity, were

often too alkaline and were too deep to meet favourable conditions for the presence of stygofauna.

1.3 SA groundwater policy and legislation

While there currently is no specific legislation in South Australia referring to stygofauna, they are indirectly

protected by a number of different acts that have been identified in detail by COOE (2014). The acts

include:

Environment Protection Act 1993;

National Parks and Wildlife Act 1972;

Mining Act 1971;

Environment Protection and Biodiversity Conservation Act 1999 (EPBC Act);

Natural Resources Management Act 2004; and

Water Allocation Plan for the Western Mount Lofty Ranges Prescribed Water Resources Area

2013.

In general, stygofauna are protected through the maintenance of groundwater habitats, protection of

threatened species of flora and fauna and the protection of biodiversity.

1.4 Geology and Groundwater

BiH mine is within the Onkaparinga River Catchment of the Western Mount Lofty Ranges and falls within

the Inverbrackie Creek Adelaidean Underground Water Management Zone. Current bores lie within the

eastern edge of the Onkaparinga River drainage system, which flows into the ocean south of Port

Noarlunga. This catchment is a fractured rock aquifer where fractures and caves were identified in the Cox

sandstone, Brighton limestone and the Tapley Hill formation. Fractures are expected to also occur in the

Tarcowie siltstone.

Stygofauna are known to be more prevalent in bores less than 10 m and with the groundwater exhibiting

specific water quality characteristics (Table 1). All bores examined are deeper than 10 m and water quality

is often outside the ideal range for stygofauna to be present.

Table 1 Groundwater conditions favourable for stygofauna and aquifer conditions at BiH.


Characteristic Reported Conditions Conducive to Stygofauna (Hancock and Boulton 2008)

Conditions of BiH Aquifers

Groundwater electrical conductivity (μScm-1) < 1500 μScm

-1 > 1500 μScm

-1

Groundwater pH (pH units) Known range: 4.3 to 7.37 units Ranges from 6.27 to 10.0

Depth of groundwater body (m) < 10 m below ground level (bgl) > 10m

Geology Presence of cavities, fractures or interstices

Present

1.5 Project Objectives

The projects objectives are the following:

1. Confirm the presence or absence of Stygofauna in 7 additional groundwater samples;

2. Provide a brief report on search effort, GW water quality for sample, geological unit; and

3. Provide items of interest and proposed distance to underground operations


2. METHODOLOGY

2.1 Sampling sites

Terramin sampled ten bores across 3 years. The sampling date and geo-referencing are provided in Table 2.

A map indicating the location of the bores, as well as other private bores in the Woodside area is provided

in Figure 2.

Table 2 Sample site and date

Bore ID Sampling Date MGA Easting MGA Northing

6628-27448 (IB1) 25/9/2014 & 26/10/2017 309059.47 6129673.69

6628-27446 (IB2) 28/9/2015 & 26/10/2017 309020.366 6129638.603

6628-27447 (IB3) 15/1/2015 309071.81 6129683.58

6628-27445 (IB4) 1/8/2017 309032.932 6129644.341

6628-27444 (IB5) 29/9/2015 & 26/10/2017 309042.03 6129652.94

6628-9156 (Cow calf) 3/11/2017 308151.1 6129887

6628-8942 (Goldwyn Ck bore) 3/11/2017 308124.761 6129978.865

6628-8945 (Gabb) 14/1/2015 & 1/8/2017 308835.526 6129305.843

6628-8939 (ONK020) 16/1/2015 308717.14 6130543.62

6628-8301 (Glatz2) 3/3/2015 309931.8 6128115

A conceptual design of the pump test bores and their relationship to the various sedimentary layers is

provided in Figure 3.

2.2 Sampling methodology

Sampling of stygofauna followed a standard protocol for all sites. The procedure initially includes installing

loggers and manually dipping surrounding bores to detect any level impacts. The bore to be pumped then

has the logger installed and is manually dipped. The pump is then installed and involves screwing 3 m

lengths of poly of 50 mm diameter into the head of the pump, then lowering and screwing in subsequent

3 m lengths of poly until desired length is reached. The desired length was determined by bore standing

water level combined with estimated drawdown caused by pumping. An exit point is established and water

is passed through a 63 μm collection net. In 2014 and 2015 water quality was then measured every minute

from a bucket after the net catching point. The pumping rate was estimated using a 20 L bucket and

determining the time for it to fill. At the completion of obtaining the desired pumping volume. The pump

was then stopped and water samples were collected for metal, ion and nutrient analysis. Contents from

the collection net were emptied into the sample container and the filled to 30% with 98% ethanol. The

sample container was then filled with bore water. In 2017 the volume sampled was much lower as any

stygofauna were expected in the upper reach of the bore. Water quality was measured once from water

pumped into a 20 L bucket after the initial purging.


Figure 2 Bore locations.


Figure 3 Conceptual design of pump test bores

Parameters measured included pH, water temperature, dissolved oxygen (DO), electrical conductivity (EC),

total dissolved solids (TDS) and turbidity. Water samples collected for metals, ions and nutrients were sent

to a NATA certified laboratory for analysis.

Stygofauna samples were processed by first adding Rose Bengal stain that makes biological material pink

in colour, providing good contrast between invertebrates, and pale sand and silt or dark organic matter in

the samples. The stain was added to the sample two days prior to sample processing. The samples where

then processed by decanting excess preservative through the 63 μm collection net. The remaining sample

was then transferred to a petri dish and examined under a Leica M80 dissecting microscope to a

magnification of 75x.


3. RESULTS

In 2014 and 2015 the volume of water sampled from the various aquifers varied greatly from a very high

69 000 L at 231086 from the Tapley Hill formation to 900 L at 6628-8945 from Tarcowie Siltstone. Physical

attributes of the groundwater bores sampled are provided in Table 3. At 231087 black sulfate bacteria

was present for first 3 hours of pumping. At ONK 20 the water turned black after 9 000 L. At 6628-8945

the water volume from 300 to 700 L black sulfate bacteria was present and cleared between 700 to 900 L.

In 2017 the volume of water sampled varied from 10 to 100 L.

Table 3 Physical attributes and type of aquifer at the groundwater bores sampled

Bore ID

(Permit/Unit

number)

Geology

formation type

Surface

elevation

(m AHD)

Screen

Depth (m

BGL)

SWL

(m)

Volume

sampled

(L)

Extraction

Depth (m) Date

6628-27448 (IB1)

Brighton limestone

454.876 203-265 45.38 29 700 60 25/9/2014

452.182 198-238 43.49 100 60 26/10/2017

6628-27446 (IB2)

Brighton limestone

452.182 198-238 41 4 476 60 28/9/2014

6628-27447 (IB3)

Cox Sandstone 454.84 108-136 44.87 3105 60 15/1/2015

6628-27444 (IB5)

Tapley Hill Formation

452.961 270-294 43.45 69000 60 29/9/2014

452.961 270-294 41.09 60 60 26/10/2017

6628-8945 (Gabb)

Perched Aquifer -Tarcowie Siltstone

408.12 open 7.56 900 15 14/1/2015

411.663 open 7.66 100 15 1/8/2017

6628-8939 (ONK020)

Tapley Hill formation

406.13 open 17.14 12 000 26 16/1/2015

6628-8301 (Glatz2)

Brachina formation

462.91 39.62-100.58

13.46 19260 60 3/3/2015

6628-9156 (Cow-calf)


399 open 6.78 10 25 3/11/2017

6628-8942 (Goldwyn Creek bore)


402.94 open 4.87 10 18 3/11/2017

6628-27445 (IB4)

Tarcowie siltstone

452.528 120-154 41.09 50 60 1/8/2017

Water quality data collected during the survey in 2014 and 2015 indicated wide varying results within and

between sites during the sampling process (Table 4). pH was most acidic at 6628-8301 although the most

acidic reading was recorded from 6628-8945. Dissolved Oxygen readings varied greatly and it is suggested

that the sampling methodology would have influenced the recordings through artificial aeration. TDS were

similar at all sites but with 6628-8301 appearing considerably higher than all other sites. Electrical

Conductivity was also the highest at 6628-8301. 6628-8939 (ONK020) was the only site to exhibit readings

that were consistently below the previously reported favourable threshold of 1.5mS/cm.


Table 4 Water Quality attributes of ground water bores at time of sampling 2014 and 2015.

Bore ID Sampling Time (mins)

Temp (oC)

pH DO (%) TDS (mg/L) EC (mS/cm)

Turbidity (NTU)

6628-27448 (IB1)

330

Min 18.86 7.12 12.9 1.13 1.77 0.7

Max 19.96 7.26 176.9 1.17 1.83 26

Average 19.68 7.14 27.28 1.15 1.8 6.08

6628-27446 (IB2)

280

Min 17.9 7.23 7.1 0.002 1.87 28

Max 22.81 8.42 125.5 1.28 2.01 239

Average 22.16 7.49 23.28 1.16 1.95 58.9

6628-27444 (IB5)

330

Min 16.96 7.49 27.9 0.822 1.36 22.5

Max 22.38 8.6 194.9 1.1 1.72 471

Average 21.37 8.04 46.59 1.03 1.62 48.67

6628-8939 (ONK020)

94

Min 16.89 6.73 29.6 0.143 0.256 15.2

Max 17.64 8.1 240.3 0.974 1.52 928

Average 17.02 6.82 58.2 0.9 1.41 106.26

6628-8945 (Gabb)

15

Min 16.9 5.07 103.7 0.008 0.012 41.8

Max 22.26 8.54 443.6 1.58 2.46 1000

Average 17.85 7.52 244.11 1.27 1.99 196.07

6628-27447 (IB3)

13

Min 16.88 9.3 79.7 0.654 1.06 64.2

Max 17.22 9.39 266.6 0.833 1.3 554

Average 17.04 9.37 114.95 0.817 1.28 135

6628-8301 (Glatz2)

125

Min 17.02 6.19 32.6 3370 5.36 25

Max 17.06 6.54 94.9 3480 5.53 54.3

Average 17.05 6.27 47.23 3419.3 5.43 35.2

Bold figures indicate readings outside favourable water quality conditions conducive to Stygofauna

Water quality measured in 2017 (Table 5) indicated that pH was outside the known range for stygofauna

at all sites with exception of Goldwyn Creek bore and Cow Calf bore. EC was measured above the known

tolerance of 1.5 mS/cm at 6628-9156 (Cow Calf bore), 6628-27448 (IB1), 6628-27446 (IB2) and 6628-27444

(IB5). Of the sites that were repeated sampling and 6628-27444 (IB5) and 6628-27446 (IB2) exhibited

higher pH and turbidity, 6628-8945 (Gabb) higher EC and lower turbidity, and 6628-27448 (IB1) higher pH.

Table 5 Water Quality attributes of ground water bores at time of sampling 2017.

Bore ID Date Temp (˚C) pH DO (mg/L) TDS (mg/L)

EC (mS/cm)

Turbidity (NTU)

6628-8942 (Goldwyn Ck bore)

3/11/2017 15.76 6.95 24.71 0.890 1.39 21

6628-9156 (Cow Calf bore)

3/11/2017 14.03 7.22 23.3 1.450 2.27 17

6628-27448 (IB1) 26/10/2017 8.32 0.959 1.62 19.7

6628-27446 (IB2) 27/10/2017 9.1 0.961 1.64 105

6628-27447 (IB3) 27/10/2017 18.85 10.0 0.606 0.94 10.7

6628-8945 (Gabb) 1/8/2017 7.64 1.400 2.55 33

6628-27445 (IB4) 1/8/2017 7.72 0.774 1.38 4.9

6628-27444 (IB5) 26/10/2017 9.08 0.849 1.46 68.1

6628-8301 (Glatz2) 27/10/2017 8.08 0.864 1.39 0.4

Bold figures indicate readings outside favourable water quality conditions conducive to Stygofauna. Blank cells indicate

measurement not taken.


Water samples collected for metal, ion and nutrient analysis are presented in Appendix 1. From the 2014

and 2015 sampling high ions were recorded at 6628-8301 (Glatz2), which is indicative of the high EC

recorded from the site. Na+ and Cl- dominated the ion concentration. High levels of Manganese were

recorded at 6628-27446 (IB2), 6628-27447 (IB3) and 6628-8301 (Glatz2). A high concentration of Total N

was recorded at 6628-27448 (IB1) with 1.0 mg/L and at 6628-8301 with 3.4 mg/L. All other readings were

below drinking water trigger values. The 2017 sampling indicated higher nutrients at 6628-27447 (IB3)

where TKN rose by over 460 %. The remaining results saw slight changes in salt concentrations reflected

in the previously observed changes in EC.

Examination of the stygofauna samples indicated no stygofauna were present in any of the samples (Table

6). While some fauna were identified they were all of terrestrial origin that is they fell into the bore,

possibly when the pump was installed.

Table 6 Stygofauna sample results.

Site Sample notes Sampling Date

6628-27448 (IB1) 1 exoskeleton of winged terrestrial insect. Sample with detritus and stones. Partial body segment of unknown origin.

25/9/2014

6628-27446 (IB2) 1 terrestrial midge (Diptera: Chironomidae). Sample with detritus and stones. Partial body segment of unknown origin

28/9/2014

6628-27447 (IB3) 1 partial terrestrial insect head. 2 terrestrial midge adults (Diptera: Chironomidae). Partial body segment of unknown origin.

15/1/2015

6628-8939 (ONK020) 1 adult terrestrial wasp (Hymenoptera). 1 terrestrial spider. Lots of silt.

16/1/2015

6628-8945 (Gabb) 1 terrestrial spider. Sample with detritus and biofilm. 14/1/2015

6628-27444 (IB5) Nothing 29/9/2014

6628-8301 (Glatz2) Nothing 3/3/2015

6628-27448 (IB1) 1 terrestrial beetle. Fine sediments and little detritus. 26/10/2017

6628-27446 (IB2) 2 terrestrial ants damaged. Fine sediments and some detritus. 26/10/2017

6628-27444 (IB5) 2 terrestrial spiders. 1 damaged terrestrial adult midge. 1 terrestrial beetle, 1 adult fly. Fine sediments and some detritus.

26/10/2017

6628-9156 (Cow calf) 1 terrestrial hemipteran, Very little detritus. 3/11/2017

6628-8942 (Goldwyn Ck

bore) 1 terrestrial spider. 1 damaged terrestrial adult midge. 1 terrestrial beetle, 1 adult fly. Little detritus.

3/11/2017

6628-27445 (IB4) 1 spider, little detritus 2/3/17

6628-8945 (Gabb) 42 Collembola, 1 spider, lots of detritus 2/3/17


4. DISCUSSION AND CONCLUSION

The conditions of the bores at BiH suggest that they not conducive to the presence of Stygofauna. Hancock

and Boulton (2008) in a study of fauna from two aquifers in Queensland and two in New South Wales

showed taxon richness decreased with distance below the water table. The most taxon-rich bores in each

region occurred where the water table depth was <10 m, were associated with the alluvium of tributaries

of large regulated river systems, and were near phreato-phytic trees. Hancock and Boulton (2008) also

indicated stygofauna were collected in water with electrical conductivity below 1.5 mg/L and a pH between

4.3 and 7.37. The groundwater in the BiH study area has either pH and EC, and sometimes both, outside

the preferred range. Additionally all the bores examined were considerably deeper than 10m.

Although Leijs (2009) had collected stygofauna across a range of aquifers, water quality and depth

information has not been published. Given small sized crustaceans such as Copepoda, Harpacticoidea, and

Ostracoda, as well as the Oligochaete worms were most commonly found, it is possible that the South

Australian stygofauana are more tolerant of higher salinities as representatives of these taxonomic groups

are often collected in saline waters. As previously stated Humphreys (2006) indicated many stygofaunas

in arid areas occur in brackish to saline waters. Roudnew et al. (2009) presented preliminary data from

bores across South Australia that is still yet to be formally published but indicated stygofauna was found

in bores with lower salinity, lesser depth and higher dissolved oxygen. Additionally the authors indicated

bacteria abundances decrease with increasing depth and corresponding increase with decreasing

dissolved oxygen.

In the current study sites it appears that there is a likely presence of microbial (bacteria and fungi)

communities that are able to derive their energy through chemical reactions with inorganic molecules such

as hydrogen sulfide, elemental sulfur and ammonia that could form the basis of simple food webs.

However, the lack of presence of rotifers or even nematodes suggests that there is lack of food for

stygofauna.

High nutrient concentrations at 6628-27448 (IB1), 6628-8301 (Glatz2) and 6628-27447 (IB3) suggest that

the groundwater might be impacted. In a previous study two geologically similar but hydrologically

partially separated aquifer systems successfully indicated elevated nitrate impacts linked to land use

activities resulted in a change in community structure (Stein et al. 2010). Within the microbial

communities, impacts from land use were mirrored by high bacterial biodiversity values atypical for

pristine groundwater of comparable systems (Stein et al. 2010).

The current sampling methodology used is a common method for sampling stygofauna. A study of the

subterranean fauna from calcrete (carbonate) aquifers of the Yilgarn Region of central Western Australia

by Alford et al. (2007) examined the effectiveness of three sampling methods. They compared the

efficiency of haul net sampling, pumping with a 12-V impeller pump, and a discrete interval sampler. No

significant taxonomic bias was detected across the sampling methods. However, sampling using a haul net

was found to be the most efficient method for capturing the available taxa per unit time when sampling

bores are less than 10 m deep, with pumping being the least efficient. Given the bores at BiH are greater

than 10 m the use of the pump appears to be the most appropriate method.


Hose and Lategan (2012) also provide sampling strategies for assessing NSW groundwater ecosystems and

they prescribe multiple samples over space and time to properly assess an ecosystem. They are also

indicate that the majority of invertebrates collected in a stygofauna sample are those in the borehole at

the time of sampling rather than being in the surrounding aquifer. Purging a bore would therefore remove

animals, which may take weeks or months to re-establish. Frequent or repeated purging for water quality

sampling interferes with stygofauna sampling, and they therefore recommend every effort be made to

coincide these activities. Species accumulation curves suggest that 10 sampling events may be necessary

in order to adequately assess the stygofauna in some locations.

For the collection of stygofauna Hose and Lategan (2012) recommend that multiple sampling events are

necessary to assess stygofauna assemblages in any bore, multiple bores per aquifer/region are needed to

assess the richness of that aquifer/region and to overcome any potential inter-seasonal variability in

stygofauna assemblages samples should be taken across at least two seasons. In the current study repeat

sampling of bores had not produced any evidence of stygofauna and therefore the prescribed sampling

protocols are not relevant in the current study area.

The historical and recent groundwater abstraction for irrigation and consumption purposes, identified the

lack of stygofauna food items, and the presence of clay aquitards (Golders 2017) within the area together

could be possible explanations of a lack of Stygofauna. The groundwater abstraction seasonally lowers the

water table reducing habitat value, and potentially removing Stygofauna. The aquitards and low

permeability rock zones, outside of groundwater bearing fractures, identified in the above mentioned

Terramin groundwater study would also prevent or slow migration of stygofauna back to an area where

they might have become locally extinct.

In conclusion, the samples examined indicated that stygofauna are not present in the BiH study area and

that current water quality and structure of the groundwater bearing fractures would prevent their

presence.


5. REFERENCES

Alford A, Steven J. B., Cooper S. J. B., Humphreys W. F. and Austin A.D. (2007) Diversity and distribution of

groundwater fauna in a calcrete aquifer: does sampling method influence the story? Invertebrate

Systematics 22(2) 127–138

Boulton A (2000) River ecosystem health down under: assessing ecological conditions in riverine groundwater

zones in Australia, Ecosystem Health 6:108 118.

COOE (2014) Care of our environment Bird-In-Hand Prefeasibility Study – Stygofauna Desktop Study Document

code: TER.BIH.20140523b Suite 613, 147 Pirie St, Adelaide, SA

Eberhard, S. (2007). Classification of Subterranean Fauna. Subterranean Ecology. Prepared for the Department of

Environment and Conservation, Western Australia, Greenwood, WA. Project 49, pp2–7.

Fradd W.P. and Morris B.J. (2015) Historical review of mine workings and production – Woodside Goldfield, Report

Book 2015/00022. Department of State Development, South Australia, Adelaide.

Golders (2017) Groundwater assessment for the native vegetation heritage agreement area. Technical

memorandum, 15 September 2017Project No. 1659870.

Goonan P., Jenkins C., Hill R. and Klenig T. (2015) Subsurface groundwater ecosystems a briefing report on the

current knowledge, monitoring considerations and future plans for South Australia. South Australia EPA

ISBN 978-1-921495-65-6

Hancock P.J. and Boulton A.J. (2009). Sampling groundwater fauna: efficiency of rapid assessment methods tested

in bores in eastern Australia. Freshwater Biology 54:902-917.

Hose G.C. and Lategan M.J. (2012) Sampling strategies for biological assessment of groundwater ecosystems CRC

for Contamination Assessment and Remediation of the Environment. Technical Report 21 ISBN: 978-1-

921431-31-9

Humphreys WF (2006). Aquifers: the ultimate groundwater dependent ecosystems. In: Eamus SL Farrer D (eds.)

Special edition on groundwater dependent ecosystems. Aust J Bot. 54:115–132

Humphreys WF (2008), 'Rising from Down Under: developments in subterranean biodiversity in Australia from a

groundwater fauna perspective', Invertebrate Systematics 22:85 101.

Leijs R (2008). Newsletter Stygofauna and Stygomicrobe, Research Flinders University,

http://www.scieng.flinders.edu.au/current/biology/msl/StygoNewsletter1.pdf

Leijs R (2009). Newsletter Stygofauna and Stygomicrobe Research, Flinders University,

http://www.scieng.flinders.edu.au/current/biology/msl/StygoNewsletter2.pdf

Menico A., K.L. Korbel K.L. and Hose G.C. (2014) River–aquifer interactions and their relationship to stygofauna

assemblages: A case study of the Gwydir River alluvial aquifer A., (New South Wales, Australia) Science of

the Total Environment 479–480: 292–305

Roundnew B, Leijis R, Seront L and Mitchell JG (2009) Biodiversity of stugofauna and stygomicrobes of aquifiers in

South Australia in relation to environmental factors. School of Biological Sciences, Flinders University,

Adelaide SA 5001. Poster presentation unpublished.

Stein H., Kellermann C., Schmidt S. I., Brielmann H., Steube C., Berkhoff S. E., Fuchs A., J€urgen Hahn H., Thulin B.

and Griebler C. (2010) The potential use of fauna and bacteria as ecological indicators. Journal of

Environmental Monitoring 12: 242–254

Terramin (2016), Bird In Hand Stygofauna, Report # BIH-ENV-004-V2. 2016.

Tomlinson, M and Bolton AJ (2010.) Ecology and management of subsurface groundwater dependent ecosystems in

Australia a review. Marine and Freshwater Research 61: 936– 949


6. APPENDICES

Appendix 1- Bore Assays

Site 6628-27445

(IB4) 6628-8945

(Gabb) 6628-27448

(IB1) 6628-27444

(IB5) 6628-27447

(IB3) 6628-27446

(IB2)

Sampling date 1/08/17 1/08/17 26/10/17 26/10/17 27/10/17 27/10/17

Total Alkalinity (mg/L) 346 372 376 265 102 223

SO4 Turb (mg/L) 42 134 1 4 - 145

Cl CDA (mg/L) 266 608 368 366 252 379

Ca DMC (mg/L) 45 106 24 2 1 2

K DMC (mg/L) 8 14 7 7 5 8

Mg DMC (mg/L) 24 66 24 15 8 32

Na DMC (mg/L) 218 369 278 289 185 353

B Diss (mg/L)

Ba Diss (mg/L)

Co Diss (mg/L)

Cu Diss (mg/L) - - 0.001 0.002 - -

Mn Diss (mg/L) 0.128 0.200 0.142 0.026 - 0.014

Mo Diss (mg/L)

Ni Diss (mg/L) - - - - - -

Pb Diss (mg/L)

Zn Diss (mg/L) 0.018 - - 0.006 - -

Fluoride (mg/L)

N Ammonia (mg/L)

N Nitrite (mg/L) - - - -

N Nitrate (mg/L) - - - 0.02

NOx Nitrite (mg/L) - - 0.01 0.02

TKN N (mg/L) - 0.5 1.4 -

N Tot (mg/L) 1.4 -

FTP P (mg/L)

P Tot (mg/L) 0.04 0.07 0.09 0.11 0.04 0.08

- Indicates values are below the detection limit

Blank cells indicated water quality parameter not measured


Appendix 1 cont. Bore Assays

Site 6628-27448 (IB1)

6628-27446 (IB2)

6628-27447 (IB3)

6628-27444 (IB5)

6628-8945

(Gabb)

6628-8301

(Glatz2)

6628-8939

(ONK020)

Sampling date 25/09/14 28/09/14 15/01/15 29/09/14 14/01/15 3/03/15 16/01/15

Total Alkalinity (mg/L) 385 289 109 310 325 384 120

SO4 Turb (mg/L) 54 230 66 106 139 119

Cl CDA (mg/L) 392 381 392 379 579 1650 325

Ca DMC (mg/L) 65 57 3 45 82 58 64

K DMC (mg/L) 8 12 8 8 12 24 7

Mg DMC (mg/L) 32 40 16 26 53 102 37

Na DMC (mg/L) 273 313 207 287 299 1070 130

B Diss (mg/L) 0.08 0.13 0.06 0.14

Ba Diss (mg/L) 0.136 0.02 0.032 0.114

Co Diss (mg/L) 0.002

Cu Diss (mg/L) 0.001 0.001

Mn Diss (mg/L) 0.079 0.236 0.189 0.151

Mo Diss (mg/L) 0.002 0.001 0.006

Ni Diss (mg/L) 0.002 0.002

Pb Diss (mg/L) 0.001

Zn Diss (mg/L) 0.027 0.013 0.017

Fluoride (mg/L) 0.8 0.9 1 0.9 0.9 0.7 0.4

N Ammonia (mg/L) 0.43 0.11 0.02 0.15 0.04 0.02

N Nitrite (mg/L) 0.02

N Nitrate (mg/L) 2.95 0.5

NOx Nitrite (mg/L) 2.97 0.5

TKN N (mg/L) 1 0.4 0.2 0.3 0.4 0.3

N Tot (mg/L) 1 0.4 0.2 0.3 3.4 0.8

FTP P (mg/L) 0.02 0.04 0.1 0.02 0.05

P Tot (mg/L) 0.06 0.03 0.05 0.02 0.11 0.07 0.06

Blank readings indicate values are below the detection limit


Appendix 2 Sample photos

Sample from GATZ2

Sample from 231086

Sample from ONK 20

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