This metadata record contains the results from 11 bioassays conducted with 2 species of Antarctic marine microalgae. Seven tests were conducted with Phaeocystis antarctica (Prymnesiophyceae), assessing the toxicity of copper, cadmium, lead, zinc and nickel. Four tests were conducted with Cryothecomonas armigera (Incertae sedis), assessing the toxicity of copper only. Test conditions for both algae are described in the excel spreadsheets. In summary, tests for P. antarctica and C.armigera, were carried out at 0 plus or minus 2 degrees C, 20:4 h light:dark (150-200 micro mol/m2/s, cool white 36W/840 globes), in natural filtered (0.45 microns for P.antarctica and 0.22 microns filtered for C. armigera) seawater (salinity - 35 ppt, pH - 8.1 plus or minus 0.2). For both species, filtered seawater was supplemented with 1.5 mg/L NO3- and 0.15 mg/L of PO43-. All tests were carried out in silanised 250-mL glass flasks, with glass lids. Test volumes for P.antartica and C.armigera were 50 mL and 80 mL, respectively. All tests consisted of 3-5 metal treatments, with 3 replicates per treatment, alongside 3 replicate controls (natural filtered seawater). Seawater was spiked with metal solutions to achieve required concentration. Concentrations tested are recorded in excel datasheets. The following replicate toxicity tests were completed for P. antarctica: - 5 tests with copper (1-20 micro g/L) - 4 tests with lead (10-500 micro g/L) - 3 tests with cadmium (100-2000 micro g/L) - 3 tests with zinc (100-2000 micro g/L) - 3 tests with nickel (200-1000 micro g/L) For C. armigera, 1 rangefinder test was carried out testing 6 concentrations (1-100 micro g/L), and 3 definitive test, with 5 concentrations (15-100 micro g/L). The age of P. antarctica and C.armigera at test commencement was 8-12 days, and 25-30 days, respectively. Algal cells were centrifuged and washed to remove nutrient rich media, and test flasks were inoculated with between 1-3 x103 cells/mL. Cell densities in all toxicity tests were determined by flow cytometry. The flow cytometer was also used to simultaneously measure change sin chlorophyll a fluorescence intensity, cell size and internal cell granularity. Toxicity tests were continued until cell densities in the control treatments had increased 16-fold. Toxicity tests with P. antarctica were carried out over 10 days, with cell densities in each replicate flask measured every 2 days. Toxicity tests with C. armigera were carried out over 23-24 days, with cell densities determined twice a week. The growth rate (cell division; u) was calculated as the slope of the regression line from a plot of log10 (cell density) versus time (h). Growth rates for all treatments were expressed as a percentage of the control growth rates. The pH in all treatments was measured on the first and last day of the test, as well as on day 6 for P. antarctica tests and an additional two times per week for C. armigera tests. Sub-samples (5 mL) for analysis of dissolved metal concentrations were taken from each treatment on days 0, 6 and 10 for P. antarctica tests, and on days 0, 7, 14, 21, and 24 for C. armigera tests. Sub-samples were filtered through an acid washed (10% HNO3, Merck) 0.45-micron membrane filter and syringe, and acidified to 0.2% with Tracepur nitric acid (Merck). All toxicity test results were calculated using measured dissolved metal concentrations, which were determined using inductively coupled plasma-atomic emission spectrometry (ICP-AES; Varian 730-ES) for Cu, Cd, Pb, Ni and Zn and using inductively coupled plasma-mass spectrometry (ICP-MS; Agilent 7500CE) for lowest concentration Cu samples (nominal concentration 1 micro g/L). Detection limits for Cu, Cd, Pb, Ni and Zn were 1, 0.12, 1.7, 1.2 and 0.1 micro g/L, respectively (ICP-AES) and 0.05 micro g/L (ICP-MS) for low concentration Cu samples. The specific growth rates (u) and corresponding measured metal concentrations were used to calculate toxicity test values using Toxcalc

This metadata record contains the results from 3 bioassays conducted with the Antarctic marine microalgae Cryothecomonas armigera (incertae sedis). These tests assessed the toxicity of copper, cadmium, lead, zinc and nickel. Test conditions for both algae are described in the excel spreadsheets. In summary, tests for P. antarctica and C.armigera, were carried out at 0 plus or minus 2 degrees C, 20:4 h light:dark (60-90 micromol/m2/s, cool white 36W/840 globes), in 80 mL natural filtered (0.22 microns) seawater (salinity - 35 ppt, pH - 8.1 plus or minus 0.2). Filtered seawater was supplemented with 1.5 mg/L NO3- and 0.15 mg/L of PO43-. All tests were carried out in silanised 250-mL glass flasks, with glass lids. Tests 1 and 2 consisted of metal treatments, with 3 replicates per treatment, alongside 3 replicate controls (natural filtered seawater). Test 3 consisted of metal treatments in an increasing series (no replicates) alongside 3 replicate controls. Seawater was spiked with metal solutions to achieve required concentration. Concentrations tested are recorded in excel datasheets as dissolved metal concentrations measured on day 0, and day 24. The average of the dissolved metal concentrations were used for further statistical analysis. The age of C.armigera at test commencement was 25-30 days. Algal cells were centrifuged and washed to remove nutrient rich media, and test flasks were inoculated with between 1-3 x10^3 cells/mL. Cell densities in all toxicity tests were determined by flow cytometry. Toxicity tests with C. armigera were carried out over 23-24 days, with cell densities determined twice a week. The growth rate (cell division; u) was calculated as the slope of the regression line from a plot of log10 (cell density) versus time (h). Growth rates for all treatments were expressed as a percentage of the control growth rates. The flow cytometer was also used to simultaneously measure changes in the following cellular parameters: chlorophyll a autofluorescence intensity (FL3), cell size (FSC) and cell complexity (SSC). The molecular stain BODIPY 493/503, was used to measure neutral lipid concentrations. Changes in cellular parameters were measured by applying a gate that captured greater than 95% of control cells in a region, R2. Changes in cellular parameters were observed in metal treatments as a shift of the cell population from the R2 region to R1 (for relative decreases) or to R3 (for relative increases). The proportion of cells in each region is expressed as a percentage of the total cell population. The pH was measured on the first and last day of the test. Sub-samples (5 mL) for analysis of dissolved metal concentrations were taken from each treatment on 24. Sub-samples were filtered through an acid washed (10% HNO3, Merck) 0.45-microns membrane filter and syringe, and acidified to 0.2% with Tracepur nitric acid (Merck). Metal concentrations were determined using inductively coupled plasma-atomic emission spectrometry (ICP-AES; Varian 730-ES) for Cu, Cd, Pb, Ni and Zn. Detection limits for Cu, Cd, Pb, Ni and Zn were 1.0, 0.3, 3.2, 1.4, and 1.0 micrograms per litre, respectively. Calculations of effect concentrations (EC 10 and 50) were made using the 'Dose Response Curve' package of R statistical analysis software. Concentration-response curves had several models applied to them, and were tested for best fit by comparing residual standard errors and Akaike's 'An Information Criterion' function . Generally, log-logistic models with 3 parameters provided the best fit. Data for each toxicity test is combined in a single excel spreadsheet, "Cryothecomonas armigera single metal toxicity". The first worksheet is titled "Test Conditions" which provides information on the toxicity test, e.g. species and metals tested, dates, test conditions, as well as explanation of abbreviations, definitions of toxicity values etc. The second worksheet includes the raw cell densities determined in each flask, the calculated growth

This metadata record contains observed and predicted toxicity data from bioassays with two species of Antarctic marine microalgae: Phaeocystis antarctica (Prymnesiophyceae) and Cryothecomonas armigera (Cercoza). Bioassay exposures were of mixtures of 5 metals at two ratios, an Environmental (ENV) and Equitoxic (EC) mixture. The measured dissolved metal concentrations were used in two mixture reference models, Independent Action (IA) and Concentration Addition (CA), to predict toxicity as population growth rate inhibition. A Flow Cytometer (BD-FACSVerse) was used to measure the density of microalgae over time, which was then converted to a growth rate. An inductively coupled plasma-atomic emission spectrometry (ICP-AES; Varian 730-ES), was used to measure metal concentrations. Data for each microalga is provided in individual excel spreadsheets, identified by the species tested. A word document is provided that contains the R code used to predict toxicity to the two microalgae by the reference models Independent Action and Concentration Addition. The R code also includes the steps required to extend the models to include a deviation parameter “a” that allows for departure from model additivity. A nested F-test then tests for significance between the fit of each test to observed toxicities. This R code has been adapted to use EC10 as parameter estimates, rather than EC50s. The code was adapted from the approach outlined in Hochmuth, J. D.; Asselman, J.; De, S. Are Interactive Effects of Harmful Algal Blooms and Copper Pollution a Concern for Water Quality Management? Water Res. 2014, 60, 41–53. DOI: 10.1016/j.watres.2014.03.041. Single-metal toxicity data and experimental protocols for P. antarctica from the following paper: and C. armigera used in this study can be found in the following papers: A robust bioassay to assess the toxicity of metals to the Antarctic marine microalga Phaeocyctis antarctica. Francesca Gissi, Merrin S. Adams, Catherine K. King, Dianne F. Jolley (2015). Environmental Toxicology and Chemistry. 2015 Feb 20. doi: 10.1002/etc.2949. Chronic toxicity of five metals to the polar marine microalga Cryothecomonas armigera – Application of a new bioassay. Darren J. Koppel, Francesca Gissi, Merrin S. Adams, Catherine K. King, and Dianne F. Jolley, (2017). Environmental Pollution, Volume 228, 2017, Pages 211-221, doi.org/10.1016/j.envpol.2017.05.034.

We investigated the toxicity of copper, zinc and cadmium to the following taxa: copepods Tigriopus angulatus (Lang) and Harpacticus sp. (Order Harpacticoida, Family Harpacticidae); flatworm Obrimoposthia ohlini (Bergendal) (Order Seriata, Family Procerodidae); bivalve Gaimardia trapesina (Lamarck) (Order Veneroida, Family Gaimardiidae); sea cucumber Pseudopsolus macquariensis (Dendy) (Order Dendrochirotida, Family Cucumriidae); sea star Anasterias directa (Koeler) (Order Forcipulatida, Family Asteriidae). Sites chosen for the collection of invertebrates for this study were free of obvious signs of metal contamination, as verified by the analysis of seawater samples from collection sites by inductively coupled plasma optical emission spectrometry (ICP-OES). Six invertebrate species were selected for toxicity tests to represent a range of taxa and ecological niches. Individuals of the copepod Tigriopus angulatus were collected using fine mesh dip nets from rock pools high on the intertidal zone. Individuals of the flatworm Obrimoposthia ohlini were collected from the undersides of boulders, high in the intertidal zone. The copepod Harpacticus sp. and bivalve Gaimardia trapesina were collected from several macroalgae species at high energy locations in the intertidal zone. Individuals of the sea cucumber Pseudopsolus macquariensis were collected from rocks from high energy locations from the intertidal to subtidal zones. Juveniles of the sea star Anasterias directa were collected from rocks in deep pools, low in the intertidal zone. All experimental tests using O. ohlini, T. angulatus, P. macquariensis and A. directa were conducted at the AAD Kingston laboratories, while some tests with Harpacticus sp. and all tests with G. trapesina were conducted in the laboratory facilities on Macquarie Island. Adult life-stages were tested for all species except for P. macquairensis and A. directa in which juvenile stages were tested. Psedopsolus macquariensis released eggs in the aquarium which developed into juveniles prior to being used in tests, and juvenile A. directa were collected from the field. Each test involved exposure to copper, zinc or cadmium solution under a static non-renewal test regime over 14 days. Five metal concentrations plus a control were used for each test, with 3-5 replicates of each concentration. Where possible, tests were replicated. Concentrations used in replicate tests sometimes varied, as species sensitivity information accrued in tests was used to optimise subsequent tests. Metal test solutions in seawater were prepared 24 hours prior to the addition of animals, using 500 micrograms/L CuSO4, 500 micrograms/L ZnCl2 and 500 micrograms/L Cd SO4 MilliQ stock solutions. Seawater was filtered to 0.45 microns and water quality parameters were measured using a TPS 90-FL multimeter at the start and end of tests. Dissolved oxygen (DO) was greater than 80% saturation, salinity 35 ppt plus or minus 0.5, and pH was ~8.1-8.3 at the start of tests. All experimental vials and glassware were acid washed with 10% nitric acid and rinsed with MilliQ three times before use. Metal concentrations were determined using ICP-OES; samples of test solutions were taken at the start (day 0) and end of tests (day 14), filtered through a 0.45 microns syringe filter and acidified with 1% ultra-pure nitric acid. Measured concentrations at the start of tests were within 96% of nominal concentrations. In order to estimate exposure concentrations, the measured concentrations at days 0 and 14 were averaged. Tests were conducted in lidded plastic vials of varying sizes, depending on the size and number of individuals in the test. For both copepod species, there were 10 individuals per 50 mL in 70 mL vials; for P. macquariensis there were 8 individuals per 50 mL in 70 mL vials; and for O. ohlini, A. directa and G. trapesina, 10 individuals per 100 mL in 120 mL vials. Tests were conducted under a light-dark regime (at 2360 lux) of 18:6h light:dark

Metadata record for data from AAS (ASAC) Project 2933. While it is generally thought that Antarctic organisms are highly sensitive to pollution, there is little data to support or disprove this. Such data is essential if realistic environmental guidelines, which take into account unique physical, biological and chemical characteristics of the Antarctic environment, are to be developed. Factors that modify bioavailability, and the effects of common contaminants on a range of Antarctic organisms from micro-algae to macro-invertebrates will be examined. Risk assessment techniques developed will provide the scientific basis for prioritising contaminated site remediation activities in marine environments, and will contribute to the development of guidelines specific to Antarctica. Amphipod and Isopod toxicity tests, Kingston 2007 Filename: Amphipod and Isopod test results.xls Test animals were collected from near shore environments at Casey Station, East Antarctica during Dec 2006 - Jan 2007, and transported to culturing facilities at the Australian Antarctic Division in Tasmania, where tests were conducted during 2007. The test animals were exposed to metals in non-renewable static tests in vials containing 50 mL of the test solution at ambient Antarctic coastal salinity of 34 ppt. Tests were held in temperature controlled cabinets (incubators) at a temperature of 0 degrees C (plus or minus approximately 1 degrees C). Five to eight test animals were introduced into each of 3 replicate vials per treatment at test commencement, and were exposed for 10 to 12 weeks during which periodic observations were made. Test solutions were renewed in weekly water changes. Periodic observations (time since start of test) are given in hr (hours), d (days) or w (weeks). At each observation time, test animals were scored in one of the Endpoint categories described on each worksheet. Each worksheet provides data for a particular test taxa (slater isopods, small red isopods, spider amphipods and Orange Long Antennae Amphipods - taxonomy to be verified) for a given test number (T01, T02) and a given metal contaminant (copper, zinc, cadmium). Test information is provided in the first 14 rows of each worksheet, e.g. Site of collection, Test start date, Endpoint categories etc. ASU = artificial settlement units (plastic scourers used by Sarah Richards, which had been deployed in Newcomb Bay in approximately the year 2000). Conc micrograms/L are nominal concentrations. Measured concentrations are provided in the worksheet: /Amph and Isop T01-02 CHEMISTRY SUMM Test temperature was 0 degrees C unless otherwise stated. Unit for all temperature data is degrees C. The file contains the following worksheets: Worksheet: /Amph and Isop T01-02 CHEMISTRY SUMM Chemistry data as provided also in Kingston 07 Chemistry_Amph and Iso.xls described below. Worksheet: /Slater isopods T01 Cu Test taxa: Slater isopod; Test ID: T01, Kingston 2007; Metal contaminant: copper Worksheet: /Slater isopods T01 Zn Test taxa: Slater isopod; Test ID: T01, Kingston 2007; Metal contaminant: zinc Worksheet: /Slater isopods T01 Cd Test taxa: Slater isopod; Test ID: T01, Kingston 2007; Metal contaminant: cadmium Worksheet: /Small red isopods T02 Cu Test taxa: Small red isopods; Test ID: T02, Kingston 2007; Metal contaminant: copper Worksheet: /Small red isopods T02 Zn Test taxa: Small red isopods; Test ID: T02, Kingston 2007; Metal contaminant: zinc Worksheet: /Spider Amphipods T01 Cu Test taxa: Spider Amphipods; Test ID: T01, Kingston 2007; Metal contaminant: copper Worksheet: /Orange LongAnt Amph T01 Cu Test taxa: Orange Long Antenae Amphipods; Test ID: T01, Kingston 2007; Metal contaminant: copper Filename:Kingston 07 Chemistry_Amph and Iso.xls Metal concentrations in test solutions were analysed using an ICP-AES, by Ashley Townsend at the Central Science Laboratory, University of Tasmania, Hobart. Worksheet: /Amph and Isop T01-02 Summary Summary of chemistry data for Amphipod and Isopod

This metadata record contains the results from bioassays conducted to show the response of the common Antarctic amphipod, Paramoera walkeri to contamination from combinations of Special Antarctic Blend (SAB) diesel, Marine Gas Oil (MGO) and Intermediate Fuel Oil (IFO 180), chemically dispersed with fuel dispersants Ardrox 6120 and Slickgone NS. Fuel only water accommodated fractions (WAF), chemically enhanced water accommodated fractions (CEWAF) and dispersant only treatments were prepared following the methods in Singer et al. (2000) with adaptations from Barron and Ka’aihue (2003). WAF was made using the ratio of 1: 25 (v/v), fuel to filtered seawater (FSW) following the methods of Brown et al. (in prep). Ratios for chemically dispersed treatments were 1: 100 (v/v), fuel to FSW and 1: 20 (v/v) dispersant to fuel. Dispersant only treatments were made using ratios for CEWAF, substituting the fuel component with FSW. Mixes were made in 5 L or 10 L glass aspirator bottles using a magnetic stirrer to achieve a vortex of 20-25% in the FSW before the addition of test media. The same mixing energy was used to prepare all WAFs for enhanced reproducibility and comparability of results (Barron and Ka’aihue, 2003). Mixes were stirred in darkness to prevent bacterial growth for 42 h with an additional settling time of 6 h at 0 plus or minus 1 oC. Extended stirring times were used following the recommendations determined as part of the hydrocarbon chemistry component of this project (Kotzakoulakis, unpublished data). A dilution series of four concentrations were made from the full strength aqueous phase of each mix using serial dilution. WAF test concentrations were 100%, 50%, 20% and 10% while CEWAF concentrations were 10%, 5%, 1% and 0.1%. These concentrations were chosen in order to quantify the mortality curve and allow statistical calculation of LC50 values. To facilitate comparisons of dispersant toxicity in the presence and absence of fuel, dispersant only test concentrations reflected those of CEWAF treatments. WAF was sealed in airtight glass bottles stored at 0 plus or minus 1 oC for a maximum of 3 h before use. Fresh test solutions were prepared every four days to ensure consistent water quality and replace hydrocarbons that adsorbed or evaporated into the atmosphere. Each test concentration was represented by five replicates with five FSW control beakers, with 10 P. walkeri individuals per replicate. Only healthy and active individuals were chosen with a size range of 7.9 plus or minus 0.7 mm for adults and 2.5 plus or minus 0.2 for juveniles measured from the base of the antennae to the widest part of the dorsal curve. Larger individuals and brooding females were not used to avoid unrelated deaths related to age or reproductive state (Sagar, 1980). Beakers were filled to 200 ml and were left open to allow the natural evaporation of lighter monoaromatic hydrocarbon components that would occur during a real spill. A small square of plankton mesh was placed in each jar to provide a substratum to reduce the stress of laboratory conditions and to help to stem cannibalism. Animals were not fed during experiments to avoid hydrocarbons adsorbed onto food pellets being ingested by the amphipods, thereby introducing an additional exposure pathway. Experiments ran for a total of 12 d exposure duration. Experiments were run in cold temperature-controlled cabinets maintained at a temperature of 0 plus or minus 1 oC, fluorescent lights in the cabinets were set to a light regime of 18 h light, 6 h darkness, following the methods in Brown et al. (2017) to reflect Antarctic summer environmental conditions. Lethal and sublethal observations were made at standard ecotoxicology test times of 24 h, 48 h, 96 h, 7 d, 10 d and 12 d, with an additional observation at 8 d coinciding with one of the 4-day water changes. The health status of each individual was classified on a scale of one to four; one showing no effect up to four being mortality.

This metadata record will contain the results of bioassays conducted to characterise the response of Antarctic near-shore marine zooplankton to hydrocarbon contaminants in Special Antarctic Blend (SAB) diesel fuels commonly used in Antarctica. The results from one summer season (2010-11) are in this record. This was conducted under the AAS Project 3054: Ecological risks from oil products used in Antarctica: characterising hydrocarbon behaviour and assessing toxicity on sensitive early life stages of Antarctic marine invertebrates. Exposure solutions of fuel were experimentally mixed by slow stir of fuel and seawater in temperature control cabinets at -1 degree C to prepare a mixture of fuel hydrocarbons in filtered seawater (FSW) termed the Water Accommodated Fraction (WAF). WAF was produced by adding fuel to seawater in 5 L or 10 L Pyrex glass bottles using a ratio of 1:24 Fuel : FSW. This mixture was stirred at slow speed with minimal vortex for 18 h on a magnetic stirrer. The mixture was settled for 6 h before the water portion was drawn from beneath the fuel. Ecotoxicological bioassays were conducted at Davis Stations in the 2010/11 summer season using SAB WAF to prepare experimental treatments consisting of WAF dilution series. For each bioassay, treatments consisted of undiluted 100% WAF and dilutions of 10%, 17%, 25% and 50% of WAFs in FSW, to test the toxicity of water accommodated fractions of these three fuels on Antarctic both the zooplankton community and single copepod species. Bioassays were conducted in open vessels (glass jars or beakers) in temperature controlled cabinets. Mortality was observed at endpoints of 24 hrs, 48 hrs, 96 hrs, 7 days, 8 days, 9 days, 10 days, 11days, 12 days, 14 days, 15 days, and 16 days. New WAF solutions were prepared at the 7 day interval to replenish the experimental treatments. Deionised water was added to test solutions as required to maintain test solution volume and salinity. Water quality data was collected at each water change. Samples of test treatments for chemical analysis of hydrocarbon concentration were taken at each water change. Results of these analyses are not included as delayed progress with HC analyses impacted on quality of samples and these data were not used. This dataset consists of Excel spreadsheets. The file name code for zooplankton bioassays is; Project number_Season_Taxa_Test name Eg AAS_3054_10-11_zooplankton_m1 Project number : AAS_3054 Season : 2010/11 season Taxa: Zooplankton Community Test name: M1 =Multi-species test 1 Bioassay spreadsheets contain the results of bioassays for a species or the zooplankton community. Where replicate tests were conducted, each experiment is on a separate worksheet. The worksheet labelled "Test conditions" shows details of Test name, dates, animal collection details, laboratory holding conditions, details of water accommodated fractions (WAF), and bioassay conditions. The worksheet labelled "Counts" has a table for each of the replicates, arranged into a column for each treatment type. These tables show the number or dead individuals which were found and removed at each of the observation days. The worksheet labelled "Totals" has calculations of total number of individuals (of all species) which were found dead at each observation day in each replicate. It also gives the mean and standard deviation for each of the treatments. Further information on the zooplankton community structure in the 6 samples taken across the summer, based on the community in the toxicity tests and trials, is also included in the spreadsheet "AAS_3054_10-11_zooplankton_CommStructure". Sampling locations were near-shore from Davis Station, Vestfold Hills and from O'Gorman Rocks, southwest of Anchorage Island and northwest of Plough Island.

Metadata record for data from AAS (ASAC) Project 2933. While it is generally thought that Antarctic organisms are highly sensitive to pollution, there is little data to support or disprove this. Such data is essential if realistic environmental guidelines, which take into account unique physical, biological and chemical characteristics of the Antarctic environment, are to be developed. Factors that modify bioavailability, and the effects of common contaminants on a range of Antarctic organisms from micro-algae to macro-invertebrates will be examined. Risk assessment techniques developed will provide the scientific basis for prioritising contaminated site remediation activities in marine environments, and will contribute to the development of guidelines specific to Antarctica. Brown Ostracod toxicity tests, Kingston 2007 Test animals were collected from near shore environments at Casey Station, East Antarctica during Dec 2006 - Jan 2007, and transported to culturing facilities at the Australian Antarctic Division in Tasmania, where tests were conducted during 2007. The test animals were exposed to metals in non-renewable static tests in vials containing 50 mL of the test solution at ambient Antarctic coastal salinity of 34 ppt. Tests were held in temperature controlled cabinets (incubators) at a temperature of 0, 2 or 4 degrees C (+/- approximately 1 degrees C). Ten test animals were introduced into each of 3 to 5 replicate vials per treatment at test commencement, and were exposed for 10 weeks during which periodic observations were made. Test solutions were renewed in weekly water changes. Periodic observations (time since start of test) are given in hr (hours), d (days) or w (weeks). At each observation time, test animals were scored in one of the Endpoint categories described on each worksheet. Each worksheet provides data for a particular test taxa (Brown Ostracods - taxonomy to be verified) for a given test number (T01, T02, T03, T04, T05,) and a given metal contaminant (copper, zinc, cadmium and lead). Test information is provided in the first 14 rows of each worksheet, e.g. Site of collection, Test start date, Endpoint categories etc. ASU = artificial settlement units (plastic scourers used by Sarah Richards, which had been deployed in Newcomb Bay in approximately the year 2000). Concentration micro grams per litre are nominal concentrations. Measured concentrations are provided in the file: Brown Ostracod_chemistry.xls, as described below. Test temperature was 0 degrees C unless otherwise stated. Unit for all temperature data are degrees C. See the readme file in the download for more information.

Metadata record for data from AAS (ASAC) Project 2933. While it is generally thought that Antarctic organisms are highly sensitive to pollution, there is little data to support or disprove this. Such data is essential if realistic environmental guidelines, which take into account unique physical, biological and chemical characteristics of the Antarctic environment, are to be developed. Factors that modify bioavailability, and the effects of common contaminants on a range of Antarctic organisms from micro-algae to macro-invertebrates will be examined. Risk assessment techniques developed will provide the scientific basis for prioritising contaminated site remediation activities in marine environments, and will contribute to the development of guidelines specific to Antarctica. Juvenile Gastropod toxicity tests, Kingston 2007 During 2007 a series of toxicity tests, using Antarctic marine invertebrates, were conducted at Australian Antarctic Division laboratories in Kingston, Tasmania, to test the sensitivity of Antarctic nearshore biota to a range of common metal contaminants. This data record describes two such tests, using juveniles of the microgastropod Skenella paludionoides. The first test (T01) was a 14 day test (start date: 20/08/2007) using juveniles less than 7 days old. The second test (T02) was a 12 week test (start date: 10/09/2007) using juveniles of the same cohort, that were less than 28 days at the commencement of the test. A range of concentrations of three single metals (cadmium, copper and zinc) were applied as test treatments to determine this species sensitivity to these common metal contaminants. T01 included all three metals, T02 used copper and zinc only. Data are provided in the excel file: CaseyKingston0607_Microgastropod.xlsx This file includes descriptive test details, test data and measured metal concentrations of test solutions. Scanned copies of laboratory notebook and test scoresheets are provided in PDF files: - CKing_ Ecotox Kingston 0607.pdf - Kingston07-microgastropod-juv-T01.pdf