oyster biomonitoring study€¦ · oysters each were deployed at eight locations with increasing...
TRANSCRIPT
HUNTER WATER
Oyster Biomonitoring Study
Burwood Beach WWTW
301020-03413 – 105
August 2013
Infrastructure & Environment
3 Warabrook Boulevard Newcastle, NSW 2304 Australia PO Box 814 NEWCASTLE NSW 2300 Telephone: +61 2 4985 0000 Facsimile: +61 2 4985 0099 www.worleyparsons.com ABN 61 001 279 812
© Copyright 2013 WorleyParsons
HUNTER WATER
OYSTER BIOMONITORING STUDY
BURWOOD BEACH WWTW
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SYNOPSIS
The Burwood Beach Oyster Biomonitoring Study was undertaken to assess the potential for effluent
and biosolids discharges to lead to bioaccumulation of chemicals in marine life, over a range of
spatial scales, using oysters as a biomonitor. A specific requirement of the study was to establish the
zone in which there is a detectable increase in the concentration of chemicals in oysters that is
related to the outfall. Concentrations of a suite of organic and metals/metalloid chemicals were
measured in Sydney rock oyster, Saccostrea glomerata, tissue following three eight week long
deployments in the receiving waters of the Burwood Beach WWTW. Three replicate cages of thirty
oysters each were deployed at eight locations with increasing distance from the Burwood Beach
outfall. Oysters were deployed in approximate north-eastern and south-western directions at
distances < 50 m (outfall), 100 m, 500 m and 2000 m from the outfall biosolids diffuser.
Concentrations of organics and metals/metalloids were compared to the Australian and New Zealand
Food Authority (ANZFA) Standards Maximum Residue Limits (MRLs) (ANZFA 2011). These were
used as a guide (in the absence of other available guidelines) rather than to assess health risks for
oyster consumption, as there are no commercially grown oysters within the boundaries of this study.
Analysis of organic chemicals included a suite of organochlorine (OC) and organophosphate (OP)
pesticides, polychlorinated biphenyls (PCBs) congeners and total PCBs (summation of PCB
congeners). There were detections of organic chemicals in oysters suggesting that Burwood Beach
WWTW was a source during some of the deployment periods. Heptachlor, trans-chlordane, cis-
chlordane and dieldrin were detected in oysters following January - April 2012 at concentrations lower
than the ANFZA MRLs (2011). Concentrations of PCB congeners and total PCB concentrations were
lower than the LOR of 0.01 mg/kg in all oysters following the three sampling events.
Assessment of metals/metalloid concentrations in oyster tissue following deployments demonstrated
that most metals/metalloids were at low concentrations. No metals/metalloids were found to exceed
the available ANFZA MRLs (2011). Concentrations of metals/metalloids were also found to be similar
to those reported as background concentrations for S. glomerata in NSW estuarine locations. There
were no significant differences in the spatial patterns of individual metals/metalloids or the multivariate
suite of metals/metalloids to suggest that oysters deployed closer to the Burwood Beach WWTW
outfalls had accumulated higher concentrations of metals/metalloids than those at sites which were
located further away.
The key objective of the Burwood Beach Oyster Biomonitoring Study was to assess the potential for
effluent and biosolids discharges to lead to bioaccumulation of chemicals in marine biota, over a
range of spatial scales, using oysters as a biomonitor. This study found that there was evidence of
bioaccumulation of OC pesticides in oysters at the outfall during one sampling event. There were no
consistent significant differences in the spatial patterns of metals/metalloids to suggest that oysters
deployed closer to the Burwood Beach WWTW had accumulated higher concentrations of these. It
would be expected that with increases in future discharges of effluent and biosolids at Burwood
Beach WWTW that higher concentrations of organic chemicals and metal/metalloids would be found
via oyster biomonitoring studies.
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Disclaimer
This report has been prepared on behalf of and for the exclusive use of Hunter Water, and is
subject to and issued in accordance with the agreement between Hunter Water and
WorleyParsons. WorleyParsons accepts no liability or responsibility whatsoever for it in respect of
any use of or reliance upon this report by any third party.
Copying this report without the permission of Hunter Water or WorleyParsons is not permitted.
HUNTER WATER
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Internal and Client Review Record
PROJECT 301020-03413 – BURWOOD BEACH OYSTER BIOMONITORING STUDY
REV DESCRIPTION ORIG REVIEW WORLEY- PARSONS APPROVAL
DATE CLIENT APPROVAL
DATE
A Draft issued for internal review
Dr K Newton / Dr M Priestley
S Codi King
11 Sept 2012 N/A
B Draft issued for internal review
Dr M Priestley
Dr K Newton
11 Sept 2012
C Draft issued for internal review
Dr M Priestley
Dr K Newton / S Codi King
16 July 2013
D Draft issued for client review
Dr M Priestley / Dr K Newton
Hunter Water / CEE
18 July 2013
E FINAL DRAFT
Dr M Priestley / Dr K Newton
EPA
August 2013
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CONTENTS
1 INTRODUCTION ................................................................................................................ 1
1.1 Burwood Beach WWTW ..................................................................................................... 1
1.1.1 Treatment Process ................................................................................................. 1
1.1.2 Environmental Protection Licence Conditions ....................................................... 1
1.1.3 Characteristics of Current Effluent and Biosolids Discharges ............................... 4
1.1.4 Effluent and Biosolids Flow Data ......................................................................... 11
1.1.5 Dilution Modeling / Dispersion Characteristics .................................................... 12
1.1.6 Biosolids Deposition ............................................................................................. 13
1.2 Burwood Beach Marine Environmental Assessment Program ......................................... 13
1.2.1 Initial Consultation ................................................................................................ 14
1.3 Study Area ........................................................................................................................ 14
1.4 Scope of Work / Study Objectives .................................................................................... 14
1.4.1 Null Hypothesis .................................................................................................... 14
1.5 Review of Previous Australian Studies ............................................................................. 15
1.5.1 Biomonitors of Chemicals in the Aquatic Environment ........................................ 15
1.5.2 Oysters as Biomonitors of Metals / Metalloids ..................................................... 15
1.5.3 Abiotic and Biotic Factors that can Influence the use of Oysters as Biomonitors of
Metals / Metalloids ............................................................................................................ 17
1.5.4 Oysters as Biomonitors of Organics .................................................................... 19
1.5.5 Abiotic and Biotic Factors that can Influence the use of Oysters as Biomonitors of
Organics ............................................................................................................................ 19
1.5.6 Biomonitoring of the Receiving Environment of Burwood Beach WWTW ........... 21
2 METHODS ........................................................................................................................ 23
2.1 Consultation / Requirements of Stakeholders .................................................................. 23
2.2 Oyster Source ................................................................................................................... 23
2.3 Oyster Deployment ........................................................................................................... 24
2.4 Spatial and Temporal Assessment ................................................................................... 26
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2.4.1 Temporal Assessment ......................................................................................... 26
2.4.2 Sampling Sites ..................................................................................................... 26
2.4.3 Replication Achieved ........................................................................................... 28
2.5 Laboratory Analysis .......................................................................................................... 29
2.5.1 Laboratory Analysis of Organics .......................................................................... 29
2.5.2 Laboratory Analysis Metals / Metalloids .............................................................. 33
2.5.3 Laboratory Quality Assurance / Quality Control ................................................... 33
2.6 Guideline Values and Comparison Criteria for Chemicals in Oyster Tissue .................... 34
2.7 Baseline Concentrations in Source Oysters ..................................................................... 37
2.8 Statistical Analysis ............................................................................................................ 37
2.8.1 Univariate Analysis .............................................................................................. 37
2.8.2 Multivariate Analysis ............................................................................................ 38
3 RESULTS ......................................................................................................................... 39
3.1 Organic Chemicals............................................................................................................ 39
3.2 Metals / Metalloids ............................................................................................................ 39
3.3 Univariate Analysis of Metals / Metalloids ........................................................................ 40
3.4 Multivariate Analysis of Metal Profiles .............................................................................. 57
3.4.1 January - April 2012 ............................................................................................. 57
3.4.2 May - July 2012 .................................................................................................... 58
3.4.3 March - May 2013 ................................................................................................ 59
3.4.4 Overall .................................................................................................................. 60
3.5 Power Analysis ................................................................................................................. 62
4 DISCUSSION .................................................................................................................... 64
4.1 Organics ............................................................................................................................ 64
4.2 Metals ............................................................................................................................... 65
5 CONCLUSIONS ................................................................................................................ 68
6 ACKNOWLEDGEMENTS ................................................................................................. 69
7 REFERENCES ................................................................................................................. 70
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Figures
Figure 1.1 Location of Burwood Beach WWTW.
Figure 1.2 Burwood Beach WWTW and outfall alignment.
Figure 1.3 Effluent and biosolids flow data for the study period (July 2011 - May 2013).
Figure 2.1 Mooring design.
Figure 2.2 Experimental design of moorings at Newcastle.
Figure 2.3 Pictures of oyster deployment moorings, oyster bags and Burwood Beach WWTW.
Figure 2.4 Locations of oyster deployments.
Figure 3.1 Concentrations of arsenic in Saccostrea glomerata tissue.
Figure 3.2 Concentrations of cadmium in Saccostrea glomerata tissue.
Figure 3.3 Concentrations of chromium in Saccostrea glomerata tissue.
Figure 3.4 Concentrations of cobalt in Saccostrea glomerata tissue.
Figure 3.5 Concentrations of copper in Saccostrea glomerata tissue.
Figure 3.6 Concentrations of iron in Saccostrea glomerata tissue.
Figure 3.7 Concentrations of lead in Saccostrea glomerata tissue.
Figure 3.8 Concentrations of manganese in Saccostrea glomerata tissue.
Figure 3.9 Concentrations of mercury in Saccostrea glomerata tissue.
Figure 3.10 Concentrations of nickel in Saccostrea glomerata tissue.
Figure 3.11 Concentrations of selenium in Saccostrea glomerata tissue.
Figure 3.12 Concentrations of silver in Saccostrea glomerata tissue.
Figure 3.13 Concentrations of zinc in Saccostrea glomerata tissue.
Figure 3.14 MDS plot of multivariate suite of metals/metalloids for each sample from the January -
April 2012 deployment.
Figure 3.15 MDS plot of multivariate suite of metals/metalloids for each sample from the May - July
2012 deployment.
Figure 3.16 MDS plot of multivariate suite of metals/metalloids for each sample from the March - May
2013 deployment.
Figure 3.17 MDS plot of multivariate suite of metals/metalloids by distance from the outfall, pooled
over deployment period.
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Figure 3.18 MDS plot of multivariate suite of metals/metalloids by deployment period, pooled over
distance from the outfall.
Figure 3.19 MDS plot of multivariate suite of metals/metalloids by direction from the outfall, pooled
over deployment period.
Tables
Table 1.1 Load limits for effluent and biosolids discharges.
Table 1.2 Summary of physicochemical, metal/metalloid and organics data in effluent collected during
2006 - 2013.
Table 1.3 Summary of physicochemical, metal/metalloid and organics data in biosolids during 2006 -
2013.
Table 1.4 Effluent and biosolids flow data for the study period (July 2011 - May 2013).
Table 1.5 Classification of zones based on prior effluent dilution modelling.
Table 2.1 GPS coordinates of oyster moorings at Burwood Beach.
Table 2.2 Deployment periods and replication achieved at each site.
Table 2.3 Organochlorine pesticides tested in oysters
Table 2.4 Organophosphate pesticides tested in oysters
Table 2.5 Polychlorinated biphenyls tested in oysters
Table 2.6 Metals and metalloids tested in oysters
Table 2.7 Comparison criteria for organic chemicals in oyster tissue.
Table 2.8 Comparison criteria for metals/metalloids in oyster tissue.
Table 3.1 Factorial GLM ANOVAs on metals/metalloids (mg/kg, wet weight) concentrations in oyster
tissue deployed during January - April 2012, May - July 2012 and March - May 2013.
Table 3.2 Regressions of oyster tissue metal/metalloids concentration with distance from the outfall
during each sampling event.
Table 3.3 PERMANOVA analysis of a suite of metals/metalloids in the Sydney rock oyster following
three deployment periods.
Table 3.3 Estimates of sample sizes required to detect a significant difference between
metals/metalloids in oysters based on power analysis of January - April 2012 sampling data
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Appendices
APPENDIX 1: Organic Chemical Concentrations in Oysters
APPENDIX 2: Metal/metalloid concentrations in Oysters
APPENDIX 3: Power Analysis
APPENDIX 4: NMI QA/QC Reports
Abbreviations
ANZFA Australian and New Zealand Food Authority
CEE Consulting Environmental Engineers
EPA Environmental Protection Authority
EPL Environment Protection License
LOR Limit of Reporting
MRL Maximum Residue Limit
MEAP Marine Environmental Assessment Program
NHMRC National Health and Medical Research Council
OC Organochlorine Pesticides
OEH Office of Environment and Heritage
OP Organophosphate Pesticides
PCBs Polychlorinated Biphenyls
WWTW Wastewater Treatment Works
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1 INTRODUCTION
1.1 Burwood Beach WWTW
The Burwood Beach Wastewater Treatment Works (WWTW) is located on the Hunter Central Coast of
New South Wales (NSW) approximately 2.5 km south of the city of Newcastle (Figure 1.1). The plant
treats wastewater from Newcastle and the surrounding suburbs, servicing approximately 185,000 people
and local industry and has an average daily dry weather flow of 44 million litres of wastewater (44 ML/d).
Over the next 30 years these flows are expected to increase to 55 - 60 ML/d, even with water
conservation measures in place.
1.1.1 Treatment Process
The secondary treatment process at Burwood Beach consists of physical screening to remove large and
fine particulates, biological filtration and waste activated sludge (biosolids) processing including aeration
and settling stages. Secondary treated effluent from Burwood Beach WWTW is discharged to the ocean
through a multi-port diffuser which extends 1,500 m offshore, with diffusers at a depth of approximately
22 m (Figure 1.2). Approximately 2 ML/d of biosolids, which is surplus to treatment requirements, is also
discharged to the ocean via a separate multi-port diffuser that extends slightly further offshore than the
effluent outfall. Both outfalls have been operating in their current configuration since January 1994.
1.1.2 Environmental Protection Licence Condi tions
The Environment Protection Licence (EPL) for Burwood Beach WWTW specifies limit conditions for the
operation of the plant. These conditions provide an indication of the characteristics of the effluent and
biosolids discharged into the ocean. Condition L1 specifies that the operation of the outfall must not
cause or permit waters to be polluted (i.e. the licensee must comply with section 120 of the Protection of
the Environment Operations Act 1997). Condition L2 specifies limits relating to total loads discharged to
the ocean (including the effluent and biosolids). These limits are provided in Table 1.1. Condition 3
specifies limits to concentrations of suspended solids and oil / grease in the effluent discharged to the
outfall. The three day geometric mean concentration limit for suspended solids is 60 mg/L and for oil /
grease is 15 mg/L. Condition 4 sets volume and mass limits of effluent and biosolids discharged via the
outfalls. The limit for effluent flow rate is 510 ML/d (to allow for higher flows in wet weather) and for
biosolids the flow limit is 5 ML/d. Daily monitoring of flow is required.
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Figure 1.1 Location of Burwood Beach WWTW.
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Figure 1.2 Burwood Beach WWTW and outfall alignment.
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Table 1.1 Load limits for effluent and biosolids discharges.
Parameter Load Limits
kg/year kg/day
Total suspended solids 4,717,189 12,924
Biochemical oxygen demand - -
Total nitrogen 778,257 2,132
Oil and grease 341,290 935
Total phosphorous - -
Zinc 3,943 11
Copper 2,080 5.7
Lead 1,472 4.0
Chromium 224 0.61
Cadmium 124 0.34
Selenium 14 0.038
Mercury 9 0.025
Pesticides and PCBs 7 0.019
1.1.3 Characteristics of Current Effluent and Biosolids Discharges
The final treated effluent and biosolids from Burwood Beach WWTW has been monitored by Hunter
Water for microbiological indicators of faecal contaminations and for a suite of metals/metalloids and
organic chemicals. A summary of this data during the period 2006 - 2013 is provided in Tables 1.2
(effluent) and 1.3 (biosolids) (data provided by Hunter Water 2013).
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Table 1.2 Summary of physicochemical, metal/metalloid and organics data in effluent collected during 2006 - 2013.
Group Parameter (units) Period N Median Mean Min Max Std
Error 75%ile 90%ile
Physicochemical Suspended solids (mg/L) 2006-13
449 27 33.6 <1 390 1.6 40 60
UV254nm Transmittance (%T) 2006-13
6 59.2 58.4 43.6 68.31 3.4 62.475 65.705
pH 2006-13
224 7.6 7.6 7 8 0.01 7.7 7.8
Total dissolved solids (mg/L) 2006-13
56 440 448.5 276 734 12.9 487.5 545
Biological Oxygen Demand - total (mg/L) 2006-13
239 23 27.4 <2 144 1.3 36 50
Chemical Oxygen Demand - Flocculated (mg/L)
2006-13
19 42 41.8 32 55 1.6 46 51.4
Grease - total high range (mg/l) 2006-13
3 <5 4.7 <5 10 2.7 6 8.4
Grease - total low range (mg/l) 2006-13
444 <2 2.7 <2 60 0.2 3 5
Ammonium nitrogen (mg/L N) 2006-13
70 23.0 21.7 1 33.1 0.8 26.8 29.4
Nitrate + nitrate oxygen (mg/L N) 2006-13
236 1.0 1.6 <0.05 14 0.1 2.1 3.7
Total Kjeldahl Nitrogen (mg/L N) 2006-13
236 26.9 26.1 2.2 48.7 0.6 33.0 36.9
Total nitrogen (mg/L N) 2006-13
236 28.7 27.6 2.45 48.7 0.6 33.6 37.7
Total phosphorus (mg/L P) 2006-13
236 2.3 2.64 0.09 8.2 0.11 3.625 4.8
Metals / Metalloids
Silver-Ag-AAS furnace (µg/L) 2006-13
31 1 3.1 <1 18 0.9 2.5 13
Silver Ag-ICP (µg/L) 2006-13
59 0.5 0.7 <1 7 0.1 0.5 1
Arsenic As-vga (µg/L) 2006-13
90 1.7 1.8 0.05 3.9 0.1 2.1 2.51
Cadmium Cd-furnace (µg/L) 2006-13
5 <1 <1 <1 <1 - <1 <1
Cadmium Cd-ICP (µg/L) 2006-13
59 <1 0.5 <1 1 <1 <1 <1
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Group Parameter (units) Period N Median Mean Min Max Std
Error 75%ile 90%ile
Chromium Cr-furnace (µg/L) 2006-13
31 1 1.9 <1 28 0.9 1.2 2
Chromium Cr- ICP (µg/L) 2006-13
59 <1 0.7 <1 2 0.1 0.75 1
Chromium Cr VI-furnace (µg/L) 2006-13
90 <1 0.7 <1 1 - 1 1
Copper Cu-furnace (µg/L) 2006-13
31 17 21.2 4 115 3.5 21 34
Copper Cu-ICP (µg/L) 2006-13
93 0.25 0.4 0.04 1.7 - 0.47 0.728
Mercury Hg-VGA ug/L) 2006-13
90 <0.1 0.1 <0.1 1.6 - <0.1 0.2
Manganese Mn-furnace (µg/L) 2006-13
31 70 76.0 31 173 6.6 82 105
Manganese-ICP (µg/L) 2006-13
59 61 63.8 27 119 2.0 67.5 80.2
Nickel Ni-furnace (µg/L) 2006-13
90 <1 <1 <1 <1 - <1 <1
Nickel Ni-ICP (µg/L) 2006-13
59 4 5.3 <1 20 0.6 5.5 13.2
Lead Pb-furnace (µg/L) 2006-13
90 3 3.1 <1 17 0.3 4 5
Selenium Se-VGA (µg/L) 2006-13
90 0.1 0.3 <0.1 2 - 0.4 0.6
Zinc Zn (µg/L) 2006-13
31 50 49.4 10 120 4.3 55 70
Zinc Zn-ICP (µg/L) 2006-13
59 24 31.2 4 164 3.2 35 55.8
Organics
Aldrin (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 - <0.01 <0.01
α-BHC Bhc-a (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 - <0.01 <0.01
β-BHC-b (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 - <0.01 <0.01
α Chlordane (ug/L) 2006-13
90 <0.01 0.000 <0.02 0.003 - <0.01 <0.01
Chlordane (ug/L) 2006-13
90 <0.01 0.001 <0.02 0.020 - <0.01 <0.01
λ Chlordane (µg/L) 2006-13
11 <0.01 0.000 <0.02 0.001 - <0.01 <0.01
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Group Parameter (units) Period N Median Mean Min Max Std
Error 75%ile 90%ile
Chlorpyrifos 2006-13
90 <0.01 0.007 <0.05 0.629 0.007 <0.01 <0.01
Lindane (µg/L) 2006-13
90 <0.01 0.000 <0.01 0.005 - <0.01 <0.01
DDT (ug/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 - <0.01 <0.01
DDD (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 - <0.01 <0.01
DDE (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 - <0.01 <0.01
Diazinon (ug/L) 2006-13
90 <0.01 0.000 <0.1 0.030 - <0.01 <0.01
Dieldrin (µg/L) 2006-13
90 <0.01 0.000 <0.01 0.012 - <0.01 <0.01
Endosulfan (µg/L) 2006-13
0 <0.01
Endosulfan-s (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Endosulfan-1 (µg/L) 2006-13
0 <0.01
Endosulfan-2 (µg/L) 2006-13
0 <0.01
Endrin (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Heptachlor (µg/L) 2006-13
90 <0.005 <0.005 <0.005 <0.005 <0.005 <0.005 <0.005
HCB (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Heptachlor-epoxide (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Methoxychlor (µg/L) 2006-13
90 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Parathion (ug/L) 2006-13
90 <0.1 0.000 <0.1 0.010 0.000 <0.1 <0.1
Total PCBs (µg/L) 2006-13
90 <0.1 <0.1 <0.1 <0.1 <0.1 <0.1 <0.1
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Table 1.3 Summary of physicochemical, metal/metalloid and organics data in biosolids during 2006 - 2013.
Group Parameter (units) Period N Median Mean Min Max Std
Error 75%ile 90%ile
Physicochemical
Total solids (%w/w) 2006-13 458 0.41 0.45 0.00 2.42 0.01 0.50 0.67
Volatile solids (%w/w) 2006-13 440 69.12 66.35 20.61 96.72 0.51 72.68 74.60
Ammonium N_Total (mg/L N) 2006-13 440 24.00 25.03 0.01 85.40 0.55 30.13 39.00
Grease – total low range (mg/L) 2006-13 440 153.5 172.0 1.0 841.0 5.5 230.0 328.2
Fluoride (mg/L) 2006-13 3 0.77 0.67 0.42 0.82 0.13 0.80 0.81
Metals / Metalloids
Silver-Ag-AASurnace (µg/L) 2006-13 152 22 23 4 63 1 29 40
Silver Ag-ICP (µg/L) 2006-13 279 11 12 0.5 38 0 15 18
Arsenic As-vga (µg/L) 2006-13 431 14.7 18.33 2.6 130 0.70 19.75 30.5
Cadmium Cd-furnace (µg/L) 2006-13 152 4 5.93 0.5 128 1.04 6 8
Cadmium Cd-ICP (mg/L) 2006-13 279 0.005 0.01 0.005 0.06 0.00 0.01 0.01
Chromium Cr VI-furnace (µg/L 2006-13 152 1 1.00 1 1 0.00 1 1
Chromium Cr_VIi-furnace (µg/L ) 2006-13 279 5 10 5 25 0.00 5 25
Chromium Cr-furnace (µg/L) 2006-13 152 46.5 68.16 1 750 7.41 68.5 105
Chromium cr- ICP (µgLl) 2006-13 279 30 50 5 3200 10 40 70
Copper Cu-furnace (µg/L) 2006-13 152 839 954 125 3930 42.8 1134 1426
Copper Cu-ICP (µg/L) 2006-13 279 830 880 5 3300 20 1000 1300
Mercury Hg- VGA ug/L) 2006-13 431 3.7 3.93 0.005 10.2 0.08 4.8 6.3
Manganese Mn-furnace (µg/L) 2006-13 152 339 360 33 1270 13.73 446.25 512.5
Manganese -ICP (mg/L) 2006-13 279 0.39 0.41 0.06 1 0.01 0.47 0.57
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Nickel Ni-furnace (µg/L) 2006-13 152 40 47.21 13 180 2.49 55 77.7
Nickel Ni-ICP (mg/L) 2006-13 279 0.03 0.04 0.005 0.33 0.00 0.05 0.07
Lead Pb-furnace (µg/L) 2006-13 152 187 224 13 900 11.37 269.25 375
Lead Pb ICP µg/L) 2006-13 279 120 130 10 450 0.01 150 212
Selenium Se-VGA (µg/L)) 2006-13 431 0.1 0.91 0.05 5.9 0.06 1.7 2.7
Zinc Zn (mg/L) 2006-13 152 2.4 3.03 0.78 15.6 0.16 3.515 5.39
Zinc Zn-ICP (mg/L) 2006-13 279 2.2 2.46 0.13 6.9 0.06 2.8 3.7
Organics
Aldrin (µg/L) 2006-13 96 0 0 0 0 0 0 0
α-BHC Bhc-a (µg/L) 2006-13 96 0 0 0 0 0 0 0
β-BHC-b (µg/L) 2006-13 96 0 0 0 0 0 0 0
α Chlordane (ug/L) 2006-13 96 0 0 0 0 0 0 0
Chlordane (ug/L) 2006-13 96 0 0 0 0 0 0 0
λ Chlordane- (µg/L) 2006-13 13 0 0 0 0 0 0 0
Chlorpyrifos (µg/L) 2006-13 96 0 0.003 0 0.239 0.003 0 0
DDT (uµ/L) 2006-13 96 0 0 0 0 0 0 0
DDD (µg/L) 2006-13 96 0 0 0 0 0 0 0
DDE (µg/L) 2006-13 96 0 0 0 0 0 0 0
Diazinon (ug/L) 2006-13 96 0 0 0 0 0 0 0
Dieldrin (µg/L) 2006-13 96 0 0.006 0 0.315 0.004 0 0
Endosulfan-s (µg/L) 2006-13 96 0 0 0 0 0 0 0
Endrin (µg/L) 2006-13 96 0 0 0 0 0 0 0
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HCB (µg/L) 2006-13 96 0 0 0 0 0 0 0
Heptachlor-epoxide (µg/L) 2006-13 96 0 0.0001 0 0.013 0.0001 0 2.8
Heptachlor (µg/L) 2006-13 96 0 0 0 0 0 0 0
Lindane (µg/L) 2006-13 96 0 0 0 0 0 0 0
Malathion (µg/L) 2006-13 96 0 0 0 0 0 0 0
Methoxychlor (µg/L) 2006-13 96 0 0 0 0 0 0 0
Parathion (ug/L) 2006-13 96 0 0 0 0 0 0 0
Total PCBs (µg/L) 2006-13 96 0 0 0 0 0 0 0
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1.1.4 Effluent and Biosolids Flow Data
Effluent and biosolids flow data for the study period was obtained from the Burwood Beach WWTW.
A summary of flow data for the period July 2011 to May 2013 is provided in Table 1.4 and Figure 1.3.
Table 1.4 Effluent and biosolids flow data for the study period (July 2011 - May 2013).
Date
Rainfall (mm)
Secondary Flow (ML)
1
By-Pass Flow (ML)
2
Total Flow (ML)
WAS (ML)
3
July 2011 238.2 2068.14 777.24 2845.38 71.66
Aug 2011 47.8 1775.64 0 1775.64 87.73
Sep 2011 136.0 1731.62 205.9 1937.52 82.86
Oct 2011 161.4 1966.85 301.27 2268.12 94.93
Nov 2011 184.5 2004.51 465.58 2470.09 86.71
Dec 2011 110.8 1825.98 6.37 1832.35 92.83
Jan 2012 53.6 1481.64 22.32 1503.96 93.38
Feb 2012 336.7 2296.60 485.42 2782.02 89.47
Mar 2012 188.0 2083.66 403.74 2487.40 96.36
Apr 2012 174.0 1889.04 306.14 2195.18 88.98
May 2012 26.2 1470.51 0 1470.51 94.01
June 2012 188.0 2255.16 373.09 2628.25 95.01
July 2012 83.5 1839.45 24.17 1863.62 86.77
Aug 2012 71.0 1704.78 62.22 1767.00 93.44
Sep 2012 16.7 1305.15 0 1305.15 87.82
Oct 2012 13.5 1257.72 0 1257.72 76.17
Nov 2012 44.6 1201.80 0 1201.80 86.92
Dec 2012 114.2 1375.59 52.98 1428.57 98.06
Jan 2013 229.0 1488.58 322.25 1810.83 99.86
Feb 2013 175.0 1855.55 397.11 2252.66 87.39
Mar 2013 241.0 1954.00 629.58 2583.58 112.08
Apr 2013 94.5 1702.77 116.92 1819.69 102.98
May 2013 60.0 1538.14 55.7 1593.84 95.64
Note 1. Secondary Flow is total secondary treated flow through the plant (i.e. total volume of screened and degritted sewage
into secondary plant over a 24 hour period from 12 midnight and discharged to ocean).
Note 2. By-Pass Flow is total volume of screened and degritted sewage which bypasses the secondary plant over a 24 hour
period from 12 midnight and is discharged to ocean.
Note 3. WAS is the Volume of Waste Activated Sludge (biosolids) pumped from the clarifier underflow over a 24 hour period
from 12 midnight and is discharged to ocean.
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Figure 1.3 Effluent and biosolids (WAS) flow data for the study period (July 2011 - May 2013).
1.1.5 Dilution Modeling / Dispersion Characteristics
Consulting Environmental Engineers (CEE 2007) calculated a predicted initial dilution for the Burwood
effluent outfall, assuming a discharge rate of 43 ML/d and all duckbill valves in operation. The model
predicted a typical dilution of 219:1 for the effluent field. Allowing for the reduction in dilution due to
the orientation of the diffuser ports parallel to the currents, initial dilution is expected to be in the range
of 180:1 to 220:1. The Water Research Lab (WRL 2007) also carried out field tests of effluent dilution
using rhodamine dye. The dilution of the surface field showed a typical dilution of 185:1. WRL (2007)
reported that the average near-field dilution was 207:1 and the 95th percentile minimum dilution was
78:1. CEE (2010) therefore considers it reasonable to base the environmental risk assessment of the
effects of effluent discharge on an effluent plume near the ocean surface with an initial dilution in the
range of 100:1 to 200:1.
The dilution of a combined biosolids and effluent discharge through the biosolids diffuser was also
calculated (CEE 2007). The CEE model predicted a typical dilution of 475:1 for discharged biosolids if
they rose to the ocean surface, or about 250:1 if trapped by stratification at mid-depth (CEE 2007).
The WRL hydrodynamic computer model showed a median dilution of 300:1, with a minimum dilution
of 100:1 when strong stratification decreases the rise and dilution of the small biosolids plumes, and a
maximum dilution at times of strong currents exceeding 1,000:1 (WRL 2007). The WRL model also
showed the biosolids plume is often trapped well below the surface by the natural stratification of the
ocean water column. WRL field tests of the biosolids plume, with dilution measured using rhodamine
dye, showed a typical dilution of 841:1. WRL reported that the average near-field dilution of the
biosolids plume was 268:1 and the 95th percentile minimum dilution was 205:1, for a submerged
plume (WRL 2007). Based on these results, it is considered reasonable to base the assessment of
the effects of biosolids discharge on two conditions; surface plume with an initial dilution of 300:1 and
submerged plume with an initial dilution of 200:1 (CEE 2010). WRL (1999) modelled the biosolids
plume at 10 m depth and showed that the centre of the plume, at about 10 m depth, the dilution
achieved is between 200:1 and 1,000:1. At a distance of 200 m from the diffuser, the dilution
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exceeds 1,000:1 and increases further with distance travelled. The diluted biosolids extends to the
south of the diffuser, but would be indistinguishable except by the sensitive techniques used in the
field studies. Based on the field tests and dilution modelling undertaken by WRL (1999, 2007) and
CEE (2007), the following mixing zones (Table 1.5) were determined for reporting purposes only.
Table 1.5 Classification of zones based on prior effluent dilution modelling.
Distance from Diffuser Zones
< 50 m outfall impact zone outfall impact
> 50 - 100 m
mixing zone
nearfield mixing zone
> 100 - 200 m midfield mixing zone
> 200 - 2,000 m farfield mixing zone
> 2,000 m reference zone reference
1.1.6 Biosolids Deposition
Previous diver inspections undertaken at the Burwood Beach outfall (i.e. by commercial divers
inspecting the outfall infrastructure) reported that biosolids deposits at the seabed can vary
significantly. In-situ diver observations have reported a biosolids thickness of 0 to 125 mm, with
variation likely a result of weather conditions. Divers have noted biosolids being washed away after
storms with no long-term accumulation on the seabed evident. More protected areas such as small
caves have a greater depth of biosolids and a peak of 750 mm was recorded in 1994/96 (note that at
this time effluent was not mixed with biosolids before discharge). ANSTO (1998) undertook a study of
the movement of seabed sediments 1,100 m south east of the outfall using iridium-radiated glass
beads. The beads were found to disperse over 100 m to the east and west and over 150 m to the
north, providing an indication of the likely expected movement of sandy sediments on the seabed. It
is expected that smaller biosolids particles would disperse at a greater rate and further than sand
particles.
1.2 Burwood Beach Marine Environmental Assessment Program
A number of monitoring programs and studies have previously been undertaken to assess the impact
of treated effluent and biosolids discharge on the marine environment at Burwood Beach (e.g. NSW
Environment Protection Authority (EPA) 1994, 1996; The Ecology Lab 1996, 1998; Australian Water
Technologies (AWT) 1996, 1998, 200, 2003; Sinclair Knight Merz (SKM) 1999, 2000; Ecotox Services
Australasia (ESA) 2001, 2005; BioAnalysis 2006; Andrew-Priestley 2011; Andrew-Priestley et al.
2012). While providing a wealth of data on the marine environment here, it is considered that these
previous studies have not effectively assessed the spatial extent and ecological significance of the
outfalls impact (CEE 2010).
The aim of the Burwood Beach Marine Environmental Assessment Program (MEAP) was to establish
the impact footprint of the existing outfall, establish the gradient of impact with distance to the edge of
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the outfall and predict the potential footprint of future impacts. A key concern of the community and
other stakeholders was the impact that the WWTW effluent and biosolids discharge has on the
bioaccumulation of toxic or harmful chemicals in marine organisms (CEE 2010). The current study
aims to address this issue by providing an assessment of the bioaccumulation of a range of
chemicals in oysters deployed in a gradient (increasing distance) from the outfall.
1.2.1 Initial Consultation
Prior to commencement of the Burwood Beach MEAP, details of the proposed sampling program and
survey methodology were discussed with Hunter Water (Client), CEE and the NSW Environment
Protection Authority (EPA) (then the Office of Environment and Heritage (OEH) (Regulator) on 10
October 2011. This meeting was undertaken to ensure that the proposed MEAP was adequate in
addressing the requirements of both the Client and the Regulator. During this meeting, any concerns
with the proposed program were raised and the methodology of the assessment program was
subsequently altered accordingly.
Prior to deployment of the mooring systems at Burwood Beach consultation with Newcastle Fishing
Co-operative, Newcastle Ports Corporation (NPC) and NSW Fisheries (Port Stephens) was also
undertaken to identify any concerns raised by commercial fisheries that operate at Burwood Beach
and in the vicinity of the study area (further detail of outcomes in Section 2.1).
1.3 Study Area
Burwood Beach is located in Newcastle, on the Hunter Central Coast of NSW (Figure 1.1). The
seabed in the vicinity of the outfall consists of small areas of low profile patchy reef, which is subject
to strong wave action and periodic sand movement, interspersed between large areas of soft
sediment habitat. These low profile reefs extend to approximately 1 m above the sand. Water depth
is approximately 22 m at the outfall diffuser. Mobile sandy sediments occur in the gutters and low-
lying seabed between reef patches. Extensive sandy beaches with intertidal rocky reef habitats occur
along the shoreline adjacent to the outfall. Merewether Beach lies to the north and Dudley Beach to
the south of Burwood Beach.
1.4 Scope of Work / Study Objectives
The key objective of the Burwood Beach Oyster Biomonitoring Study was to assess the potential for
effluent and biosolids discharges to lead to bioaccumulation of chemicals in marine biota, over a
range of spatial scales, using oysters as a biomonitor. A specific requirement of the study was to
establish the zone in which there is a detectible increase in the concentration of chemicals in oysters
that is related to the Burwood Beach outfall.
1.4.1 Null Hypothesis
The hull hypothesis was:
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There is no significant difference in the level of chemicals in the tissue of oysters deployed
at sites located at a range of distances from the Burwood Beach WWTW outfall.
1.5 Review of Previous Australian Studies
1.5.1 Biomonitors of Chemicals in the Aquatic Environment
Environmental chemicals, such as metals/metalloids, polychlorinated biphenyls (PCBs),
organochlorines (OC) pesticides and organophosphorus (OP) pesticides may enter the sewage
treatment process via domestic and industrial sources. Incomplete removal during sewage treatment
can result in entry into the aquatic environment via sewage effluent release. Once released into the
aquatic environment, chemicals may dissolve in seawater or bind to particulates or sediments.
Aquatic biota may then take up chemicals through direct ingestion of water, particulates or food
(Naimo 1995). Uptake by aquatic biota is of concern due to potential toxicity effects on biota but also
associated human health concerns. Thus, routine biomonitoring of metals/metalloids and organic
chemicals in the aquatic environment is required.
Biomonitoring of metals/metalloids, PCBs and pesticides in seawater or sediments can sometimes
pose difficulties. Chemicals in seawater are often at low concentrations, below limits of analytical
detection. Another consideration is that release of chemicals is not constant but instead likely to be
dependent on pulse releases into the aquatic environment. To address these issues, biological
monitors (biomonitors) have been used to monitor chemicals in the aquatic environment. In
particular, molluscs have been shown to be useful and able to bioaccumulate chemicals that reflect
concentrations from the surrounding environment. They have also been used because it is the
chemicals that are bioavailable that are of most concern and can impact aquatic organisms.
Assessing concentrations in oysters provides a direct indication of what chemicals are bioavailable
and have the potential to cause harm.
The use of molluscs to measure chemicals includes the successful development of the Mussel Watch
programme (Goldberg et al. 1983) and, in Australia, the Sydney rock oyster, Saccostrea glomerata, is
the predominant molluscan species used for biomonitoring of heavy metals/metalloids (Avery et al.
1996; Scanes 1996; Lincoln-Smith and Cooper 2004; Robinson et al. 2005). Oysters have also been
used for biomonitoring of organics in the marine environment (Ajani et al. 1999; NSW EPA 1996;
Scanes 1996). This species has also been for biomonitoring of organics in the marine environment
(Ajani et al. 1999; NSW EPA 1996; Scanes 1996) but not as frequently.
1.5.2 Oysters as Biomonitors of Metals / Metalloids
In the aquatic environment, molluscs may be exposed to metals/metalloids through direct ingestion of
water or food sources (Naimo 1995). Following uptake of chemicals, the organism may excrete, bind
to a biomolecule and / or store within tissues. Also, in the case of essential metals (i.e. copper, zinc
and iron)they can be used for essential metabolic processes (Rainbow 2002). One of the concerns of
uptake of metal/metalloids by biota is the potential toxicity effects on the organism. In molluscs,
potential effects due to metal/metalloid exposure includes reproductive and growth impairments,
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behavioural abnormalities and in some cases, mortality (Keller and Zam 1991; Naimo 1995; Norris
and Carr 2006). A second concern is the potential environmental persistence of metals and
metalloids. Metals/metalloids have the potential to bioaccumulate in biota and bio-magnify through
the food chain. Consumption of biota that has elevated concentrations of metals/metalloids presents
a concern for human health. Thus, routine biomonitoring of metals/metalloids in the aquatic
environment is required.
Molluscs, in particular oysters, have been established to be used as biomonitors of metals/metalloids.
There have been a range of laboratory studies undertaken that demonstrate how oysters are capable
of bioaccumulating metals/metalloids. Eisler et al. (1972) found that the Atlantic oyster (Crassostrea
virginica) bioaccumulated cadmium to greater concentrations than was recommended for human
consumption (13 mg/kg), despite residing in waters with a concentration lower than that
recommended for safe drinking (0.1 µg/L). Further, Watling (1983) demonstrated that the Pacific
oyster (Crassostrea gigas), exposed to 100 µg/g (wet weight) of chromium, cadmium and lead for
three weeks bioaccumulated up to 3.5, 11 and 27 fold, respectively, metal concentrations in controls.
In the same study, Watling (1983) found that essential metals, copper and zinc, bioaccumulated in
C. gigas, although the rate of bioaccumulation was lower in comparison to non-essential metals, such
as chromium, cadmium and lead. Following three weeks exposure to 100 µg/g (wet weight) copper
and zinc, concentrations in C. gigas tissue were 2 and 1.1 fold that of controls.
The capacity of oysters to bioaccumulate metals/metalloids, which reflect environmental
concentrations, has resulted in their widespread use as biomonitors of bioavailable metals/metalloids
in aquatic environments. In Australia, S. glomerata, is commonly used for biomonitoring of heavy
metals/metalloids in the marine environment (Avery et al. 1996; Scanes 1996; Spooner et al. 2003;
Lincoln-Smith and Cooper 2004; Robinson et al. 2005; Andrew-Priestley 2011; Andrew- Priestley
2012). For example, Brown and McPherson (1992) used Saccostrea glomerata (then known as S.
commercialis) to assess spatial and temporal changes in copper and zinc throughout the Georges
River (NSW, Australia) and observed that metal concentrations increased with distance from the
mouth of the estuary, with an increase of 40% for copper and 300% for zinc concentrations from 1975
compared to 1987. Further, Spooner et al. (2003) analysed wild Saccostrea glomerata (then known
as S. commercialis) and found that concentrations of zinc and copper were significantly elevated in
oysters which were grown in an Australian contaminated location, Botany Bay, (2600 ± 690 μg/g for
zinc and 170 ± 45 μg/g for copper) compared to oysters grown at reference locations, Jervis Bay and
Batemans Bay (which ranged from 980 ± 400 μg/g to 1793 ± 392 μg/g for zinc and 22 ± 14 μg/g to 65
± 18 μg/g for copper).
Scanes (1996) also demonstrated that S. glomerata, was a useful biomonitor of metal contamination
in waters adjacent to wastewater treatment outfalls in Sydney, NSW. The concentrations of
metals/metalloids were reduced following the commissioning of deepwater offshore discharge.
Where oysters are used to monitor chemicals in the receiving environment of sewage effluent
discharge it is likely that exposure to effluent, and any potential chemicals contained in the effluent, is
not constant but fluctuates with environmental conditions and plume dynamics. Importantly, studies
have shown that oysters are capable of bioaccumulating metals and maintaining their tissue
concentrations (Nielsen and Hrudey 1983; Luoma et al. 1985; Boisson et al. 2003).
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1.5.3 Abiotic and Biotic Factors that can Influence the use of Oysters
as Biomonitors of Metals / Metalloids
Many factors can influence the rate of metal/metalloid uptake by biota and potentially contribute to
variability among or within studies, sites and individuals, even those which employ the same species
as a biomonitors. This could include factors that are biological such as age, sex, size, feeding,
gonadal development and / or pre-exposure history to metals (Ayling 1974; Boening 1999) or
environmental such as organic carbon, sediment composition, temperature, pH, dissolved oxygen
and / or hydrologic features such as oceanic currents and sewage plume dynamics (Elder and Collins
1991).
DEPLOYMENT PERIODS
Deployment periods should be sufficient to allow for metal/metalloid equilibrium in oyster tissue.
Equilibrium is defined as the time that it takes for biomonitors to reach environmental concentrations.
Biomonitors should be deployed for a period which is sufficient for all metals to reach equilibrium in
the tissue. One of the ways to adequately address equilibrium in the tissues is to understand the
rates of uptake and depuration (whereby oysters in clean water remove metals/metalloids from their
tissue). Metals/metalloids have been estimated to take three to twelve weeks to equilibrate in oyster
tissue (Watling 1983; Scanes and Roach 1999).
Essential metals are those which have roles in metabolic functioning, certain quantities of these
metals are required to meet metabolic needs and these metals cannot be immediately detoxified or
excreted. Although oysters are considered to be effective biomonitors of all heavy metals (Phillips
and Rainbow 1989; Scanes 1996), the equilibrium time may be longer for essential metals. Thus,
non-essential metals/metalloids may have higher potential for bioaccumulation and provide relative
concentrations in tissues which more closely reflect environment loads, in comparison to essential
metals including copper, zinc and iron.
Deployment and exposure periods should be selected that are appropriate in terms of timeframe for
metal uptake of both essential and non-essential metals. However, this can sometimes be a trade off
with being able to maintain the experiment. It is difficult to maintain oyster deployments in the marine
environment, due to potential issues relating to sea conditions, tampering or removal of oysters by
humans and interference by marine wildlife (i.e. shark consumption).
BACKGROUND METAL AND METALLOID CONCENTRATIONS
Metals/metalloids are natural elements of the environment. Different oyster populations can have
different metal and metalloid concentrations due to natural variation in environmental background.
Spatial variation in metal/metalloid concentrations poses difficulties in the measurement of metals and
metalloids and the capacity to differentiate between background concentrations and elevated
concentrations due to anthropogenic input (Phillips and Rainbow 1993; Cantillo 1997; Scanes and
Roach 1999). Scanes and Roach (1999) calculated background heavy metal concentrations for
S. glomerata for twelve locations in NSW which were identified as having a low risk of metal
contamination. Care must be taken though, as these locations were estuarine (as opposed to the
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marine location used in the current study), but this provides a baseline indication for metals/metalloids
expected in NSW.
MORPHOLOGY AND GENETIC MAKE-UP
Many factors can influence bioaccumulation of metals in oysters including age, size, reproductive
condition, tissue type and genetic make-up (i.e. such as triploid versus diploid).
Different populations of oysters may have different rates of uptake or responses for metals/metalloids.
For example, Robinson et al. (2005) demonstrated that two different populations of oysters sourced
from two close sites (both within the Clyde River) had significantly different (p < 0.05) zinc
concentrations. This demonstrates that care should be taken comparing different populations and
studies. Oysters should be sourced from a single population or sufficient replication should be used
to assess natural variability between populations.
Robinson et al. (2005) investigated how factors can influence metal uptake. They measured a suite of
metals (including copper, cadmium, zinc, lead and selenium) in S. glomerata from two
uncontaminated estuaries and five estuaries known to have elevated metals. In particular, age and
tissue type were found to be highly influential. Oysters aged three years had significantly higher
tissue metal concentrations compared to those one year old. They also found a significant difference
between tissue types, with the mantle tissue bioaccumulating the highest concentrations of the five
metals.
Reproductive condition can be an issue if oysters spawn during a biomonitoring program. This is
because during peak reproductive condition, a large proportion of an oyster‟s body weight is gonadal
tissue (up to 60%) which is lost during spawning (Cox et al. 1996), however individuals can spawn
different amounts and not always at the same time. Thus, results may have higher variability if
comparing individuals where spawning has occurred for some individuals during the biomonitoring.
Oysters should be selected from a similar size, age and population to help minimise sources of
variations. Oysters that are selected from a single population, and then deployed to the locations, will
eliminate the variability that is associated with different ages and populations. Oysters should be
selected from a similar size class, and additional measurements of weight and condition index can
help to account for variation among sizes. Using a composite sample (pooled sample of individuals)
rather than individuals will also assist with reducing variability. Robinson et al. (2005) recommends
using at least six oysters.
In addition, the timing of deployments should avoid the period when spawning is likely to occur.
Although the timing of spawning varies from year to year, it is usually during mid-February to late
March for S. glomerata along the mid north NSW coast of Australia.
ANALYSIS METHODS
The moisture content of an oyster affects the wet weight of the organism and thus influences the final
calculation of chemicals per unit mass of the tissue. The measurement of chemicals in tissue is
generally undertaken in dried tissue eliminating this issue; otherwise the percentage of moisture can
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be reported or accounted for as an additional factor in analyses. Using composite samples should
also assist with minimising variation.
1.5.4 Oysters as Biomonitors of Organics
Molluscs are also considered to be effective biomonitors of organic chemicals in the aquatic
environment (Scanes 1996, 1997; Ajani et al. 1999; Andrew-Priestley 2011, Andrew-Priestley et al.
2012), although in Australia this has been studied to a much lesser extent compared to oyster
biomonitoring of metals/metalloids due to the high lipid content in oysters which is known to interfere
with organic chemical analyses.
The majority of Australian literature on field of studies biomonitoring for organics has focused on fish
or other invertebrates, such as abalone. There have been several studies using oysters. Scanes
(1997) undertook field studies to demonstrate that the Sydney rock oyster, S. glomerata, is capable of
bioaccumulating OC pesticides (including chlordane, dieldrin, heptachlor epoxide, PCBs, DDT, DDD
and DDE) from contaminated locations. Detectable concentrations of all organics were present in S.
glomerata tissue after three days deployment. Concentrations of organics in tissue were highest
following 209 days, although the large majority of bioaccumulation occurred quickly. After 209 days
the oysters were transported to a clean location to monitor rates of depuration of organics. Biological
half-lives (a measure of depuration) were relatively fast and ranged from four days (heptachlor
epoxide) to 46 days (DDT). Deployment of S. glomerata was also useful in demonstrating a
significant reduction in OC contamination of waters adjacent to nearshore sewage treatment outfalls
in Sydney, NSW, Australia, following commissioning of deep-water offshore discharge (Scanes 1996).
1.5.5 Abiotic and Biotic Factors that can Influence the use of Oysters
as Biomonitors of Organics
DEPLOYMENT PERIODS
Biomonitors should be deployed for a period which is sufficient for organics to reach equilibrium in the
tissue, which varies considerably between different compounds. It is necessary to understand the
rates of uptake and depuration of each organic contaminant. Scanes (1997) deployed S. glomerata
from clean waters into a known contaminated location (Long Bay, Sydney) and measured tissue
organic concentrations (mg/L, wet weight) at numerous intervals throughout the deployment which
lasted 209 days. Based on this information, estimates were provided of the time required for
equilibrium (time required for oyster tissue to reach environmental concentrations) of organics based
on their graphs of tissue organic concentrations. It was reported that equilibrium in S. glomerata took
three to twelve days for dieldrin, twelve to twenty days for chlordane, seventy two days for DDT and
twelve to twenty days for PCBs (Scanes 1997). If oysters are not deployed for a sufficient time to
allow organics to equilibrate then oyster tissue concentrations may not be a true representation of
environmental concentrations or organics may be „missed‟ and below the limit of reporting (LOR).
Another consideration is that if exposure to organics fluctuates then oysters may depurate (i.e.
remove) for some organics. Where oysters are used to monitor organics in the receiving environment
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of sewage effluent discharge it is likely that exposure to effluent, and any potential chemicals
contained in the effluent, is not constant but fluctuates with environmental conditions and plume
dynamics. In the same study outlined above, Scanes (1997) demonstrated that the biological half-life
varied considerably between different organics in S. glomerata. Half-lives were estimated as four
days for heptachlor epoxide, twelve days for dieldrin, twenty-four days for chlordane, forty-six days for
DDT and eighty-one days for PCBs (Scanes 1997). The relatively long half-lives of organics suggest
that they should remain elevated in oyster tissue even if there are fluctuations between contaminated
and clean waters.
Oysters should be deployed for a sufficient time to allow for organic equilibrium in tissues. However,
this can sometimes be a trade off with being able to maintain the experiment. In particular, it is
difficult to maintain oyster deployments in the marine environment, due to potential issues relating to
sea conditions, tampering or removal of oysters by humans and interference by marine wildlife. The
above studies suggest that eight weeks should be an appropriate deployment period for the
equilibrium of the majority of OC and OP pesticides and PCBs.
MORPHOLOGY AND GENETIC MAKE-UP
Many factors can influence bioaccumulation of organics in oysters including age, size, reproductive
condition, tissue type and genetic make-up (i.e. such as triploid versus diploid). There is not an
extensive amount of literature characterising how these factors may influence organic uptake by
oysters. However, it is likely that some or all of these factors would also be influential as sources of
variability on organic bioaccumulation by S. glomerata, i.e. it is likely that oysters of different ages and
sizes have different rates of organic uptake.
Reproductive condition is an important consideration for biomonitoring of organics in oysters. In
comparison to other tissue types, the gonad of an oyster is higher in lipids and likely to bioaccumulate
higher concentrations of organics. During peak reproductive condition, a large proportion of the body
weight of an oyster is gonadal tissue (up to 60%) which is lost during spawning (Cox et al. 1996).
Thus, if oysters spawn then the fraction of the body weight (which is most likely to have higher
organic concentrations compared to other tissues) is lost. Further, within a single population,
individuals can spawn different amounts and not always at the same time. In addition, the results
may have higher variability if comparing individuals where spawning has occurred for only some
individuals during the biomonitoring.
ANALYSIS METHODS
Organics are lipid soluble chemicals and it has been suggested that the proportion of lipids should be
accounted for in biomonitoring studies. This could include measurement of lipids to ensure there is
low variability between individuals/samples or, as recommended by Connell (1988), reporting organic
concentrations per unit weight of lipids (rather than tissue). Scanes (1998) demonstrated that organic
tissue concentrations strongly correlate with the percentage of lipids in S. glomerata. In contrast,
Scanes (1996) found no correlation between lipids and organics and suggested this was due to lower
organic concentrations. The National Oceanic and Atmospheric Administration (NOAA 1989) also
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found that there were no correlations between lipids and PCBs, DDT, lindane and PAHs and weak
correlations for chlordane and dieldrin.
It is suggested that the measurement of lipids could be accounted for through measurement and
inclusion as a co-factor or by reporting results as per unit of lipids, particularly in studies of highly
contaminated areas. Alternatively, using composite samples should also assist with minimising this
variation between samples.
1.5.6 Biomonitoring of the Receiving Environment of Burwood Beach
WWTW
Several studies have been conducted at Burwood Beach WWTW to assess chemical
bioaccumulation in oysters (following short term deployment periods in the receiving waters), resident
fish, final treated sewage effluent and sediments. The Hunter Environmental Monitoring Program
(Hunter EMP) was conducted between 1992 - 1996 (Ajani et al. 1999; NSW EPA 1996) to assess OC
pesticides, PCBs and metals/metalloids in deployed oysters and sediments. Oysters, S. glomerata,
were deployed in the receiving waters of Boulder Bay WWTW, Burwood Beach WWTW and at four
reference locations (Point Stephens, Boat Harbour, Redhead and Terrigal) for three months at a time,
with subsequent measurements of metals/metalloids (arsenic, cadmium, chromium, cobalt, copper,
lead, manganese, mercury, nickel, selenium, silver and zinc) and OCs (aldrin, BHC, lindane, technical
chlordane, Dieldrin, DDD, DDE, DDT, endosulfan, endrin, heptachlor, hexachlorbenzene,
methoxychlor, oxychlordane and PCBs). Deployments were repeated eight times during 1992 - 1994,
with three deployments prior to and five following the commissioning of the extended Burwood Beach
and Boulder Bay WWTWs.
Within oysters, only technical chlordane (a mixture of 23 chlordane isomers and related compounds),
DDE and DDD were detected (out of the seventeen organochlorines monitored) and none of these
were in oysters deployed in waters near Burwood WWTW. Technical chlordane was detected once in
August 1991, in oysters deployed at Boulder Bay, at a concentration of 0.02 mg/kg. Concentrations
ranged from 0 - 0.0142 mg/kg for technical chlordane, 0 - 0.0011 mg/kg for DDE and
0 - 0.0008 mg/kg for DDD. All measurements of DDD were below the LOR, apart from August 1992
where it was detected in samples from all locations. Redhead was the only location where mean
concentrations of DDD exceeded the LOR of 0.02 mg/kg. For sediments, there were no OC
pesticides detected at Burwood Beach, although trace concentrations were detected at some of the
reference locations.
Within sediments, all metals/metalloids were comparable to background levels at the Burwood Beach
location. For oysters, selenium at Burwood Beach was the only metal which was higher than the
ANZFA MRLs (ANZFA 2011). A possible explanation provided was that natural levels of selenium
are higher within this region, however it was concluded that further investigation was required. For
metals/metalloids it was found that there was high variability and there were no clear patterns with
metal/metalloids concentrations and locations. One of the major outcomes of this study was the
recommendation that an impact versus control comparison was not suitable for Burwood Beach.
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Several changes in treatment technology to Burwood WWTW have occurred during and since the
study of NSW EPA (1996).
More recently, BioAnalysis (2007) performed an assessment of OC pesticides and metals/metalloids
in sediments from the Burwood Beach outfall. No OC pesticides were detected in sediments from
Burwood Beach or at any of the reference locations. Metal/metalloid concentrations in sediments
were also low and apart from manganese (which ranged from ~ 45 to 75 mg/kg at Burwood Beach) all
reference locations had higher concentrations in comparison to the Burwood Beach WWTW sampling
location. All metals/metalloids were below the ANZECC trigger guidelines (ISQ-Low) (BioAnalysis
2007).
In 2008, metals/metalloids from the Burwood Beach WWTW were analysed in Sydney rock oysters,
S. glomerata, which were deployed for 6 weeks in effluent receiving waters (Burwood near: < 50 m
and Burwood far: > 150 m) and at reference locations (Redhead and Fingal Island) at depths of 4, 8
and 12 m (Andrew-Priestley 2011). Results of this study showed concentrations of most heavy
metals/metalloids were not significantly different (p > 0.05) in the tissue of S. glomerata deployed at
Burwood Beach compared to those at the reference locations (Fingal Island and Redhead). All
metals fell below the ANFZA MRLs (ANZFA 2011) except for arsenic (1.24 mg/kg compared to
ANZFA MRL of 1 mg/kg). With the exception of nickel, selenium and lead, mean concentrations of
metals in the study were considerably lower than NSW median background concentrations
determined by Scanes and Roach (1999) both at impact and reference locations. Nickel, selenium
and lead concentrations in oyster tissue were higher than those reported by Scanes and Roach
(1999) at both impact and reference locations. Comparisons to historic data (HWC 1990 and NSW
EPA 1996) suggested that, via measurement in oyster tissue, metal concentrations released into the
marine environment via sewage effluent from Burwood Beach WWTW have not changed from earlier
studies; however, further investigation is underway to determine present levels in the marine
environment. Findings suggested that S. glomerata was a suitable biomonitor for heavy
metals/metalloids in Australian waters.
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2 METHODS
2.1 Consultation / Requirements of Stakeholders
Prior to deployment of the mooring systems at Burwood Beach consultation with the EPA (then OEH),
Newcastle Fishing Co-operative, Newcastle Port Corporation (NPC) and NSW Fisheries (Port
Stephens) was undertaken to identify any concerns raised by commercial fisheries that operate at
Burwood Beach and in the vicinity of the study area. A number of requirements were identified and
suggestions made as listed below:
To assess stakeholders‟ concerns, large surface buoys with flashing lights (SLB800 with
SL60 lights) were used for the study and moorings were placed outside shipping channels.
As requested, GPS co-ordinates of all moorings were provided to NSW Maritime, NSW
Fisheries, NPC and Newcastle Fisherman‟s Co-op following the deployment.
Oysters were placed at a depth of ~ 3 m to allow survival of the oysters and reduce the
potential for accidental damage / loss by recreational vessels.
NSW Fisheries and Marine Parks permits were required for this study and have been
obtained for this activity (Fisheries Permit P11/0051; Marine Parks Permit 2011/046).
The EPA suggested that the three replicate cages on each mooring should be separated
by a distance of 30 m (i.e. a long line arrangement would be needed). It was not
considered that this arrangement would be suitable or feasible for this study, firstly due to
the distance of each mooring from each other (i.e. two at the outfall and two within 100 m of
the outfall), the risk to recreational boating and fishing activities and the logistical
constraints in doing this (i.e. issues with keeping all replicate oyster cages at the same
required level / depth, additional surface or subsurface buoys would be required, additional
lines and moorings).
Insurance against losses was addressed by having an extra mooring deployed at the
outfall. For the first sampling event, the extra samples from the outfall were required be
tested for metals only to determine whether there was a difference in exposure to effluent /
sludge around the outfall. If no difference were found these samples would simply act as
insurance for all the following surveys. If significant differences were found, these samples
would be sampled for all parameters in the following rounds.
2.2 Oyster Source
Oysters were obtained from a commercial oyster farmer, XL Oysters (located at Tea Gardens, within
Port Stephens estuary). Oysters were depurated in clean water for two weeks prior to deployment.
Oysters were sourced from the same population and all individuals were of a similar size and
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approximately 2 years of age. Sex was not determined as studies have indicated there is not likely to
be a difference between sexes in S. glomerata bioaccumulation of chemicals (Robinson et al. 2005).
2.3 Oyster Deployment
The deployment of the mooring systems and oysters at Burwood Beach was carried out by
McLennan‟s Dive Services. Oysters were deployed at a depth of 3 m (selected based on the plume
dynamics outlined in WRL 2007) using buoyed moorings of oysters in UV resistant mesh cages.
Oysters were deployed for ~ 8 weeks with biannual sampling events over a 2 year period (resulting in
four sampling periods in total). For each sampling period, three (replicate) mesh cages of oysters
(containing thirty oysters per bag) were deployed at each of the locations for a period of 8 weeks. A
schematic of a mooring system is provided in Figure 2.1, the experimental design is presented in
Figure 2.2 and pictures are shown in Figure 2.3.
Figure 2.1 Mooring design.
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Figure 2.2 Experimental design of moorings at Newcastle.
Figure 2.3 Pictures of oyster deployment moorings, oyster bags and Burwood Beach WWTW.
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2.4 Spatial and Temporal Assessment
2.4.1 Temporal Assessment
Oysters were deployed for a period of eight weeks. Four deployments were undertaken over a two
year period. Deployments were undertaken from (1) 31 January to 2 April 2012, (2) 22 May to 9 July
2012, (3) 16 October to 18 December 2012 and (4) 26 March to 22 May 2013. The exposure period
of eight weeks was selected based on the time required for equilibration but also a suitable
deployment period to minimise the risk of oyster mortalities, loss of moorings and / or oyster bags.
Prior studies have shown that eight weeks has been sufficient deployment / exposure time for oysters
to equilibrate metals (Scanes 1998; Boisson et al. 1998, 2003) and organics (Scanes 1997) to that of
the environmental / exposure concentrations. Due to the low recovery of oyster bags during October
- December 2012, this deployment period was not included in the results (see Section 2.4.3).
2.4.2 Sampling Sites
Oysters were deployed at seven sites at range of distances from the outfall in an approximate NE /
SW direction; 0 m (outfall A and B), 100 m NE and SW, 500 m NE (A and B) and SW and 2,000 m NE
and SW (Figure 2.4). The seven sampling sites were distributed along the known dispersion
pathway (WRL 2007) of the plume in order to establish a gradient of exposure. As insurance against
potential losses, one extra mooring was deployed at the Burwood Beach outfall site and at 500 N (i.e.
a total of nine moorings). GPS co-ordinates of all sampling sites are provided in Table 2.1.
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Figure 2.4 Locations of oyster deployments.
Table 2.1 GPS coordinates of oyster moorings at Burwood Beach.
Location Site Distance from
outfall (m)
Direction Latitude (S) Longitude (E)
Outfall Impact
Outfall A 0 Outfall 32°58.176' 151°45.102'
Outfall B* 0 Outfall 32°58.163' 151°45.104'
Midfield Mixing Zone
100 N 100 NE 32°58.128' 151°45.168'
100 S 100 SW 32°58.209' 151°45.076'
Farfield Mixing Zone
500 N A 500 NE 32°57.978' 151°45.356'
500 N B* 500 NE 32°58.020' 151°45.364'
500 S 500 SW 32°58.369' 151°44.896'
Reference 2000 N 2000 NE 32°57.402' 151°46.040'
2000 S 2000 SW 32°58.981' 151°44.472'
* Added as insurance moorings.
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2.4.3 Replication Achieved
During this study there were a number of oyster bags that went missing following deployment. The
actual replication that was achieved at each site during each sampling event is summarised in Table
2.2. During the first two sampling events, nearly all replicates were recovered. However, this was not
the case during October - December 2012 or March - May 2013.
During the October - December 2012 sampling event, a large number of oyster bags were missing
including all replicates from the outfall and all northern sites. A 1 m length of rope was used to attach
oyster bags to the mooring chain. This rope was woven through the three bags and secured with two
knots and multiple cable ties. At all these oyster moorings, the rope that attached the bags was not
cut and hanging loose (suggesting that the rope was untied from the mooring). Based on this, it was
suspected that these losses were due to tampering with oyster moorings (as it would have been
impossible for the ropes to come loose otherwise). Due to the low level of replication achieved, this
sampling event was not tested or included in the results.
During the March - May 2013 sampling event, the oyster bags were attached in a similar way as
described above, except that a stainless steel wire was intertwined with the rope and knots making it
difficult to remove the bags without stainless steel cutters. At all oyster moorings, except for 100 m N
and 500 m N A, there were only two bags available. For the missing replicates, the bags were
attached but there were holes in the bottom corners. On all these bags, the holes were not a clean
straight cut and this may suggest that these losses were due to interference by a marine mammal or
fish (i.e. chewing open bags to access the oysters inside).
Table 2.2 Deployment periods and replication achieved at each site.
Site Deployment Period & Number of Cages Retrieved
Jan - April 2012 May - July 2012 Oct - Dec 2012 March - May 2013
Outfall A 3 3 0 2
Outfall B 3 3 0 2
100 N 3 3 0 3
100 S 3 3 2 2
500 N A 3 3 0 3
500 N B* 0 3 0 0
500 S 3 3 3 2
2000 N 3 2 0 2
2000 S 3 2 3 0
Note: variations from planned replication are highlighted in bold.
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2.5 Laboratory Analysis
Each bag of oysters was treated as a replicate and a composite sample of ten individual oysters per
bag was used for analysis (n = two or three bags per site). Oysters were removed from sample bags,
opened, composited, homogenized then analysed by the National Measurement Institute (NMI),
which is a NATA accredited laboratory in the processing of biological tissue samples for chemical
analyses. Samples were collected using the following quality control procedures:
Initially oysters (consisting of three composite samples of ten oysters / site) were collected
from the proposed source (XL oysters) and analysed for the suite of chemicals to confirm
the source was suitable – these were named “time zero”;
“Time zero” oysters (three replicate samples of ten oysters each, collected at the start of
each deployment from the oyster population) were included in each sampling round;
During deployments, oysters were collected by a qualified marine scientist, transferred
(using gloves) into pre-labelled snap lock bags, frozen overnight (-20ºC) and placed into a
clean esky on ice for delivery. No shucking or sub-sampling of oysters was undertaken in
the field to prevent contamination of tissue samples;
Samples were sent to the laboratory under standard chain of custody (COC) conditions and
removed from sample bags, sub sampled and analysed by NMI following their sampling
protocols for marine tissue samples.
2.5.1 Laboratory Analysis of Organics
Organochlorine (OC), organophosphate (OP), total polychlorinated biphenyls (PCBs) and PCB
arochlors were analysed by NMI using their method for Determination of Organochlorine Pesticides,
Organophosphorus Pesticides (OPPs) and Polychlorinated Biphenyls (PCBs) in Biota (method NR19,
NMI 2008b) (Tables 2.3 - 2.5). Whole oyster tissue (wet weight) was homogenised in a blender and
mixed with anhydrous sodium sulphate then extracted using dichloromethane. The extract was
cleaned up by Gel Permeation Chromatography (GPC). The final extract was analysed by Gas
Chromatography - Electron Capture Detector (GC-ECD) (dual column) for OC and PCBs and Gas
Chromatography - Nitrogen/Phosphorus Detector (GC-NPD) for OP compounds. For every batch of
twenty samples or less, at least one blank, one duplicate, one blank spike, one sample spike and one
laboratory control sample (CRM or in-house reference) was tested.
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Table 2.3 Organochlorine pesticides tested in oysters.
Sample
and Matrix
Individual Test Test Limit of Reporting
(LOR)
Method Reference
Whole
Oyster
Tissue
(wet
weight,
mg/kg)
Organochlorine
Pesticides (OCs)
Bromophos-ethyl 0.01 mg/kg
NR19
Carbophenothion 0.01 mg/kg
NR19
Chlorfenvinphos (E)
and (Z)
0.01 mg/kg
NR19
Chlorpyrifos 0.01 mg/kg
NR19
Chlorpyrifos-methyl 0.01 mg/kg
NR19
Demeton-methyl 0.01 mg/kg
NR19
Diazinon 0.01 mg/kg
NR19
Dichlorvos 0.01 mg/kg
NR19
Dimethoate 0.01 mg/kg
NR19
Ethion 0.01 mg/kg
NR19
Fenamiphos 0.01 mg/kg
NR19
Fenthion 0.01 mg/kg
NR19
Malathion 0.01 mg/kg
NR19
Azinphos Methyl 0.01 mg/kg
NR19
Monocrotophos 0.01 mg/kg
NR19
Parathion 0.01 mg/kg
NR19
Parathion-methyl 0.01 mg/kg
NR19
Pirimphos-ethyl 0.01 mg/kg
NR19
Prothiofos 0.01 mg/kg
NR19
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Table 2.4 Organophosphate pesticides tested in oysters.
Sample
and Matrix
Individual Test Test Limit of Reporting
(LOR)
Method Reference
Whole
Oyster
Tissue
(wet
weight,
mg/kg)
Organophosphat
e Pesticides
(OPs)
Aldrin 0.01 mg/kg
NR19
Alpha- BHC 0.01 mg/kg
NR19
Beta- BHC 0.01 mg/kg
NR19
2, 2- DDD 0.01 mg/kg
NR19
4,4-DDE 0.01 mg/kg
NR19
4,4-DDT 0.01 mg/kg
NR19
DDT (total) 0.01 mg/kg
NR19
Dieldrin 0.01 mg/kg
NR19
Alpha endosulfan 0.01 mg/kg
NR19
Beta endosulfan 0.01 mg/kg
NR19
Endosulfan sulphate 0.01 mg/kg
NR19
Endosulphan (total) 0.01 mg/kg
NR19
Endrin 0.01 mg/kg
NR19
Endrin aldehyde 0.01 mg/kg
NR19
Endrin ketone 0.01 mg/kg
NR19
Heptachlor 0.01 mg/kg
NR19
Heptachlor epoxide 0.01 mg/kg
NR19
Hexachlorobenzene
(HCB)
0.01 mg/kg
NR19
Gamma-BHC 0.01 mg/kg
NR19
Methoxychlor 0.01 mg/kg
NR19
Cis-chlordane 0.01 mg/kg
NR19
Trans-chlordane 0.01 mg/kg
NR19
Chlordane (total) 0.01 mg/kg
NR19
Oxychlordane 0.01 mg/kg
NR19
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Table 2.5 Polychlorinated biphenyls tested in oysters.
Sample
and Matrix
Individual Test Test Limit of Reporting
(LOR)
Method Reference
Whole
Oyster
Tissue
(wet
weight,
mg/kg)
Polychlorinated
Biphenyls (PCB)
Congeners
# 8 0.01 mg/kg
0.002 mg/kg for the
April - May 2013
deployment.
NR19
NR19
# 18 0.01 mg/kg
NR19
# 28 0.01 mg/kg
NR19
# 44 0.01 mg/kg
NR19
NR19
# 52 0.01 mg/kg
0.002 mg/kg for the
April - May 2013
deployment.
NR19
# 66 0.01 mg/kg
NR19
# 77 0.01 mg/kg
NR19
NR19
# 101 0.01 mg/kg
NR19
# 105 0.01 mg/kg
0.002 mg/kg for the
April - May 2013
deployment.
NR19
# 118 0.01 mg/kg
NR19
NR19
# 126 0.01 mg/kg
NR19
# 128 0.01 mg/kg
NR19
# 138 0.01 mg/kg
0.002 mg/kg for the
April - May 2013
deployment.
NR19
NR19
# 153 0.01 mg/kg
NR19
# 169 0.01 mg/kg
NR19
# 170 0.01 mg/kg
NR19
NR19
# 180 0.01 mg/kg
0.002 mg/kg for the
April - May 2013
deployment.
NR19
# 187 0.01 mg/kg
0.002 mg/kg for the
April - May 2013
deployment.
NR19
# 195 0.01 mg/kg
NR19
NR19
# 206 0.01 mg/kg
NR19
# 209 0.01 mg/kg
NR19
Total
Polychlorinated
Biphenyls (PCBs)
Total sum of
congeners
0.01 mg/kg
NR19
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2.5.2 Laboratory Analysis Metals / Metalloids
Metals/metalloids were analysed by NMI using their method for Determination of Elements in Food
and Biota (method NT2.46, NMI 2012) (Table 2.6). Whole oyster tissue (wet weight) was
homogenised in a blender. The sample was digested with concentrated nitric acid (or a mixture of
nitric and hydrochloric acids) by heating on top of a boiling water bath. Elements were determined
using Inductively Coupled Plasma - Mass Spectrometry (ICP - MS) and / or Inductively Coupled
Plasma - Atomic Emission Spectrometry (ICP - AES). The choice of analytical technique depended
on the required detection limit and the need to avoid interferences. For every batch of twenty
samples or less, at least one blank, one duplicate, one blank spike, one sample spike and one
laboratory control sample (CRM or in-house reference) was tested.
Table 2.6 Metals/metalloids tested in oyster tissue samples.
Sample
and Matrix
Individual Test Test Limit of Reporting
(LOR)
Method Reference
Whole
Oyster
Tissue
(wet
weight,
mg/kg)
Metals/metalloids Arsenic 0.05 mg/kg NT2_46
Inorganic arsenic 0.05 mg/kg NT2_56
Cadmium 0.01 mg/kg NT2_46
Chromium 0.05 mg/kg NT2_46
Cobalt 0.01 mg/kg NT2_46
Copper 0.01 mg/kg NT2_46
Iron 0.01 mg/kg NT2_46
Lead 0.01 mg/kg NT2_46
Manganese 0.01 mg/kg NT2_46
Mercury 0.01 mg/kg NT2_46
Nickel 0.01 mg/kg NT2_46
Selenium 0.01 mg/kg NT2_46
Silver 0.02 mg/kg NT2_46
Zinc 0.01 mg/kg NT2_46
2.5.3 Laboratory Quality Assurance / Quality Control
For every batch of twenty samples or less, at least one blank, one duplicate, one blank spike, one
sample spike and one laboratory control sample (CRM or in-house reference) was tested. Quality
assurance and quality control (QA/QC) procedures employed by the analytical laboratory (National
Measurement Institute, NMI) are listed below:
NMI has National Association of Testing Authorities (NATA) accreditation and Quality
System certification in accordance with ISO 9001 and ISO 17025;
Every twenty samples, an analysis blank (containing solvent used to extract chemicals)
was tested;
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Every twenty samples, a laboratory control sample (spiking of known concentration of
measured analyte) was undertaken. The acceptable range for spike recoveries was 50 -
150%;
Every ten samples, a sample was duplicated to test the replication between sample runs.
Acceptable relative percentage differences on duplicates was 40%;
Every twenty samples a matrix spike (containing analyte concentrations which were
unknown to the analyst and different to that being tested) was undertaken. The acceptable
range for spike recoveries was 50 - 150%. Acceptable relative percentage differences on
spikes were 40%.
The percentage of moisture in oysters was analysed following the December 2012 -
January 2013 and April - May 2012 deployments. Ideally, concentrations of metals should
be adjusted by the percentage of moisture and reported in dry weight concentrations but
this was not possible as this information was not available during all sampling events.
However, the percentage of moisture was similar between sites and sampling events. The
percentage of moisture for December 2012 - January 2013 ranged from 85 - 88.8%, with
an average of 86.86% and the percentage of moisture for April - May 2012 ranged from 84
- 87.7%, with an average of 85.51%.
For each sampling round, a quality control report was provided by NMI. The report was reviewed to
ensure quality control blanks, duplicates and spikes were within acceptable ranges as outlined above.
Copies of the QA/QC reports for each sampling event are provided in Appendix 4.
2.6 Guideline Values and Comparison Criteria for Chemicals in Oyster Tissue
A summary of available guidelines for maximum residues of organic and metal/metalloid chemicals in
a) saltwater used for aquaculture production, and b) oysters sourced from NSW background
concentrations is provided in Tables 2.7 and 2.8.
Maximum residue levels (ANZFA 2011) were used for comparison to assess whether chemicals were
present at concentrations of concern. These guidelines have been used as a point of comparison in
other studies that have used S. glomerata as a biomonitor of oysters in the receiving waters of
Boulder Bay and Burwood Beach (for example, Andrew-Priestley 2011; Ajani et al 1999; NSW EPA
1996).
Note: Maximum residue levels (ANZFA 2011) are not applicable to this study in terms of health risks
for human consumption of oysters as the main aim of this study was to use oysters as a biomonitor
for environmental contamination, not to assess whether chemicals exceed concentrations in oysters
intended as a food source. There are no oysters commercially grown within the boundaries of this
study. However, in the absence of other available guidelines the ANZFA MRLs are used as a point of
comparison to assess whether metals are elevated.
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Metal/metalloid concentrations in oysters were compared to those in time zero oysters to determine
whether concentrations had changed following the eight week deployments.
Background metal/metalloid concentrations reported by Scanes and Roach (1999) were also used for
comparison. Background metal concentrations are expected in environmental samples, such as
oysters, as metals/metalloids are natural constituents of the environment. Background concentrations
of individual metals/metalloids can vary between locations, according to the natural geology of the
region. Scanes and Roach (1999) provide an indication of the background metal concentrations in
S. glomerata found in 20 estuaries throughout NSW.
Note: The study undertaken by Scanes and Roach (1999) was based on measurement of
metals/metalloids in S. glomerata sampled from uncontaminated estuaries through NSW. There may
be differences between estuaries and marine environments in background levels of metals/metalloids.
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Table 2.7 Comparison criteria for organic chemicals in oyster tissue.
a ANZFA (2011),
b Scanes and Roach (1999).
Contaminant ANZFA (2011) Food Standards: Maximum Residue Limits
for molluscs (mg/kg, wet weight) a
Organochlorine Pesticides (OCs)
Aldrin 0.1
Alpha-BHC 0.01
Alpha-Endosulfan NA
Beta-BHC 0.01
Beta-Endosulfan NA
Cis-Chlordane 0.05
Delta-BHC 0.01
Dieldrin 0.1
Endosulfan Sulfate NA
Endrin NA
Endrin Aldehyde NA
Endrin Ketone NA
gamma-BHC (Lindane) 1
Heptachlor 0.05
Heptachlor epoxide 0.05
Hexachlorobenzene (HCB) 0.1
Methoxychlor NA
Oxychlordane 0.05
pp-DDD 1
pp-DDE 1
pp-DDT 1
Trans-Chlordane 0.05
PCBs
Total PCBs < 0.5
Organophosphate Pesticides (OPs)
Azinphos (Ethyl) NA
Azinphos (Methyl) NA
Chlorfenvinphos (E) NA
Chlorfenvinphos (Z) NA
Chlorpyrifos NA
Chlorpyrifos Methyl NA
Demeton-S-Methyl NA
Diazinon NA
Dichlorvos NA
Dimethoate NA
Ethion NA
Fenitrothion NA
Fenthion NA
Malathion NA
Parathion (Ethyl) NA
Parathion (Methyl) NA
Pirimiphos (Ethyl) NA
Pirimiphos (Methyl) NA
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Table 2.8 Comparison criteria for metals/metalloids in oyster tissue.
Metals / metalloids
ANZFA Food Standards: Maximum Residue Limits for molluscs
(mg/kg, wet weight) a
Concentrations in NSW oysters from background / reference locations
(mg/kg, wet weight) b
Arsenic < 1.0 1.88
Cadmium < 2.0 0.54
Chromium NA 0.26
Cobalt NA 0.064
Copper NA 21.6
Iron NA -
Lead < 2.0 0.085
Manganese NA 2.53
Mercury < 0.5 -
Nickel NA 0.13
Selenium 1.0 0.4
Silver NA 0.24
Zinc 1000 277
a ANZFA (2011),
b Scanes and Roach (1999).
2.7 Baseline Concentrations in Source Oysters
Prior to the first oyster deployment, two oyster composite samples (aggregates of ten oysters) from
the proposed oyster source (XL oysters, Port Stephens) were tested for the same suite of analytes to
ensure that the source was appropriate for the study. All OC pesticides, OP pesticides, PCB
congeners and PCBs were below the limit of reporting (LOR) and a summary of the results is
provided in Appendix 1.
Background trace metal concentrations are expected in environmental samples, such as oysters, as
metals are natural elements of the environment. Background concentrations of individual metals can
vary between locations, according to the natural geology of the region. Scanes and Roach (1999)
provide an indication of the background metal concentrations in S. glomerata found in 20 estuaries
throughout NSW. Concentrations of trace metals/metalloids were well below national food authority
maximum residue level for oysters (ANZ MRLs) (ANZFA 2011) and oyster background concentrations
for NSW (Scanes and Roach 1999). The analysis demonstrated that XL oysters were a suitable
oyster source for the Burwood Beach Oyster Biomonitoring Study.
2.8 Statistical Analysis
2.8.1 Univariate Analysis
Statistical analyses were performed using Statistica Version 7. Chemical concentrations in oyster
tissue were examined for normality, using a normal probability plot and homogeneity of variance,
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using a means versus standard deviation test and the data transformed (ln x+1) where applicable.
Where chemicals were below the LOR, half the LOR was used. Differences in concentrations of
metals/metalloids in oyster tissue over all deployments were assessed using a general linear model
factorial ANOVA with time and site as the main factors. An interaction between time and site was
also assessed. In the case of some metals (including cobalt, iron, lead, manganese, nickel and
silver), a normal distribution could not be achieved using a log transformation. These metals were
instead analysed via univariate PERMANOVAs in Primer 6, which computes a randomisation p-value
and does not rely on data being normally distributed.
Linear regression was also used for each deployment period to determine if there were significant
gradient relationships (p < 0.05) between chemicals and distance from Burwood Beach WWTW
outfall. While the relationship between oyster metal bioaccumulation is not necessarily a linear
relationship, regression should still show if tissue concentrations of each metal/metalloid was related
to site distance from the outfall. The results for cobalt and nickel in August - September 2012 and
arsenic and cobalt in April - May 2013 did not meet normality assumptions and were unable to be
transformed. These metals were instead analysed using permutational linear regression (Butler et al.
2003) which randomises cases and provides a distribution free test. It was also used when standard
regression p-values were very close to 0.05 and more evidence was required to confirm a statistical
relationship. In all cases 999 randomisations were performed.
2.8.2 Multivariate Analysis
Multi-Dimensional (MDS) plots were generated in PRIMER 6 to identify if there was any grouping
between sites in metal profiles during each sampling event. Ordination of metal concentrations was
performed using MDS scaling in PRIMER 6, based on ranked matrices of dissimilarities between
samples, employing the square root transformation Euclidean distance, as a measure of dissimilarity.
Goodness of fit (stress) was assessed using Kruskal‟s stress formula and compared to maximum
values recommended by Sturrock and Rocha (2000).
Analysis of similarities (ANOSIM) was undertaken in PRIMER 6 to assess if there was a significant
difference in metal profiles. If a significant difference was found, pairwise comparisons were
performed to assess which pairwise site comparisons were contributing to the difference.
Power analysis was undertaken on the first round of data in order to help design and modify, where
applicable, future oyster bioaccumulation studies. A Type I error rate of 5% (0.05) was adopted here,
and a Type II error rate of 20% (0.2, power 80%) was considered acceptable. A 50% effect size was
used. A 50% effect size has been considered suitable in other studies that have used S. glomerata
as a biomonitor (Robinson et al. 2005).
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3 RESULTS
3.1 Organic Chemicals
Analysis of organic chemicals included a suite of organochlorine (OC) and organophosphate (OP)
pesticides, polychlorinated biphenyls (PCBs) congeners and total PCBs (summation of PCB
congeners). Following the January - April 2012 deployment, OC pesticides were detected at Outfall B
and 2000 S. At Outfall B, four chemicals were detected at or above the LOR including heptachlor,
trans-chlordane, cis-chlordane and dieldrin (with respective averages of 0.009 mg/kg, 0.028 mg/kg,
0.007 mg/kg and 0.007 mg/kg). Trans-chlordane was detected in oysters from 2000 S at an average
concentration of 0.085 mg/kg. These concentrations are below the ANZFA MRLs (ANZFA 2011) of
0.05 mg/kg for heptachlor, trans-chlordane and cis-chlordane and 0.1 mg/kg for dieldrin. All other
organic chemicals were below the LOR.
For the May - July 2012 deployment and the March - May 2013 deployment, all OCs, OPs, PCB
congeners and total PCBs were lower than the LOR (0.01 mg/kg).
A summary table of organic concentrations detected in oyster tissue, with comparison to ANZFA
MRLs for molluscs (ANZFA 2011) is provided in Appendix 1. As the majority of organics were below
the LOR, statistical comparisons were not carried out.
3.2 Metals / Metalloids
Metals/metalloids in oyster tissue, including arsenic, cadmium, chromium, cobalt, copper, iron, lead,
manganese, nickel, selenium, silver and zinc are presented in Figures 3.1 - 3.13. These graphs also
include comparisons to the available ANZFA MRLs (ANZFA 2011), concentrations of
metals/metalloids that have been previously detected in NSW estuarine background locations and
concentrations in time zero samples (i.e. oysters before each deployment). The full results of
metals/metalloids that were detected in oyster tissue, along with comparison to the ANFZA MRLs,
concentrations of metals/metalloids in S. glomerata from background locations in NSW (Scanes and
Roach 1999) and time zero concentrations (i.e. before deployment) is also provided in Appendix 2.
Where arsenic exceeded 1 mg/kg, these oysters were tested for inorganic arsenic. Inorganic arsenic
is the portion of total arsenic that is inorganic and includes the most toxic forms, arsenite (As3+
) and
arsenate (As5+
). All samples tested for inorganic arsenic were below the LOR of 0.05 mg/kg and the
ANZFA MRL of 1 mg/kg. ANFZA MRLs are also available for cadmium (2 mg/kg), lead (2 mg/kg),
mercury (0.5 mg/kg), selenium (1 mg/kg) and zinc (1000 mg/kg). All oyster tissue samples were well
below these limits.
Most metal/metalloid concentrations were lower than or similar to those reported by Scanes and
Roach (1999) for oysters from NSW background estuarine locations. Concentrations of copper,
selenium and zinc were higher across most sites and of a similar magnitude spatially.
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Prior to deployment, oysters were tested for metals/metalloids (time zero), to compare whether
concentrations changed after each deployment period. It was found that following each deployment
most metals/metalloids (including arsenic, cadmium, chromium, copper, lead, mercury, nickel,
selenium, silver and zinc) had higher values in field deployed oysters in comparison to the respective
time zero oysters for that deployment.
3.3 Univariate Analysis of Metals / Metalloids
General linear model ANOVAs or univariate PERMANOVAs were used to assess for significant
differences in oyster tissue metal/metalloid concentrations among times and sites to determine if
there were significant interactions between time and site. The results of these ANOVA analyses are
provided in Table 3.1.
Overall, there were no patterns to show consistent significant spatial variability of any metals along a
distance gradient or between sites (i.e. there were no metals that were consistently elevated over the
three sampling events at outfall sites or that decreased with distance from the outfall).
For many metals, including arsenic, cadmium, cobalt, iron, manganese, silver and zinc, there were
significant interactions found between time and site indicating that the patterns among sites were
inconsistent between deployment periods. Patterns in arsenic, cobalt, iron and silver were
inconclusive and there was high temporal variability and spatial variability between sites. The
patterns for cadmium and zinc suggest that values were different across most sites following one
deployment, in comparison to the other two sampling events. Cadmium concentrations were lower
during May - July 2012 with the exception of samples collected at 2000 S. Concentrations of zinc
were higher during March - May 2013, except at outfall B. For manganese and lead, during March -
May 2013 concentrations were different at both outfall sites in comparison to other sites. During
March - May 2013, manganese concentrations were significantly elevated at the outfall sites in
comparison to the 500 m and 2000 m sites, but lead concentrations were significantly lower at the
outfall sites in comparison to all other sites. A significant main effect was found for the factor of time
for nickel and selenium, whereby concentrations were higher during March - May 2013 in comparison
to January - April 2012 and May - July 2012.
Linear regressions were used to determine if there were any significant relationships between metal
concentrations and distance from the outfall, for each deployment period. Cadmium was found to
significantly decrease with distance from the outfall during January - April 2012 but significantly
increased with distance during March - May 2013. Iron significantly decreased with distance from the
outfall during May - July 2012 and March - May 2013. Manganese was also found to significantly
decrease with distance from the outfall during March - May 2013.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
2
1
0
Ars
en
ic (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
2
1
0
Ars
en
ic (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall B
Outfall A100m S
500m S2000m S
TIME ZERONSW BG
2
1
0
Site (distance from outfall)
Ars
en
ic (
mg
/k
g)
LOR
LOR = 0.02 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.1 Concentrations of arsenic in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.50
0.25
0.00
Ca
dm
ium
(m
g/
kg
)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.50
0.25
0.00
Ca
dm
ium
(m
g/
kg
)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.50
0.25
0.00
Site (distance from outfall)
Ca
dm
ium
(m
g/k
g)
LOR
MRL = 2.0 (mg/kg) LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.2 Concentrations of cadmium in S. glomerata tissue (mg/kg, wet weight) following
eight weeks offshore deployment during January - April 2012, May - July 2012 and March - May
2013 (mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters /
replicate. LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.2
0.1
0.0
Ch
rom
ium
(m
g/
kg
)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.2
0.1
0.0
Ch
rom
ium
(m
g/
kg
)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.2
0.1
0.0
Site (distance from outfall)
Ch
rom
ium
(m
g/
kg
)
LOR
January - April 2012
May - July 2012
March - May 2013
LOR = 0.05 (mg/kg)
Figure 3.3 Concentrations of chromium in S. glomerata tissue (mg/kg, wet weight) following
eight weeks offshore deployment during January - April 2012, May - July 2012 and March - May
2013 (mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters /
replicate. LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.08
0.04
0.00
Co
ba
lt (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.08
0.04
0.00
Co
ba
lt (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.08
0.04
0.00
Site (distance from outfall)
Co
ba
lt (
mg
/k
g)
LOR
LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.4 Concentrations of cobalt in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
30
15
0
Co
pp
er
(mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
30
15
0
Co
pp
er
(mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
30
15
0
Site (distance from outfall)
Co
pp
er
(mg
/k
g)
LOR
May - July 2012
LOR = 0.01 (mg/kg)
March - May 2013
January - April 2012
Figure 3.5 Concentrations of copper in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
30
15
0Iro
n (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
30
15
0Iro
n (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
30
15
0
Site (distance from outfall)
Iro
n (
mg
/k
g)
LOR
LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.6 Concentrations of iron in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.08
0.04
0.00Lea
d (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.08
0.04
0.00Lea
d (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.08
0.04
0.00
Site (distance from outfall)
Lea
d (
mg
/k
g)
LOR
MRL = 2.0 (mg/kg) LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.7 Concentrations of lead in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
2
1
0
Ma
ng
an
ese
(m
g/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
2
1
0
Ma
ng
an
ese
(m
g/
kg
)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
2
1
0
Site (distance from outfall)
Ma
ng
an
ese
(m
g/
kg
)
LOR
LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.8 Concentrations of manganese in S. glomerata tissue (mg/kg, wet weight) following
eight weeks offshore deployment during January - April 2012, May - July 2012 and March - May
2013 (mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters /
replicate. LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.010
0.005
0.000
Merc
ury
(m
g/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.010
0.005
0.000
Merc
ury
(m
g/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.010
0.005
0.000
Site (distance from outfall)
Merc
ury
(m
g/k
g)
LOR
MRL = 0.5 (mg/kg) LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.9 Concentrations of mercury in S. glomerata tissue (mg/kg, wet weight) following
eight weeks offshore deployment during January - April 2012, May - July 2012 and March - May
2013 (mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters /
replicate. LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.30
0.15
0.00Nic
ke
l (m
g/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.30
0.15
0.00Nic
ke
l (m
g/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.30
0.15
0.00
Site (distance from outfall)
Nic
kel (m
g/k
g)
LOR
LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.10 Concentrations of nickel in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.50
0.25
0.00
Sele
niu
m (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.50
0.25
0.00
Sele
niu
m (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.50
0.25
0.00
Site (distance from outfall)
Sele
niu
m (
mg
/k
g)
LOR
MRL = 1.0 (mg/kg) LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.11 Concentrations of selenium in S. glomerata tissue (mg/kg, wet weight) following
eight weeks offshore deployment during January - April 2012, May - July 2012 and March - May
2013 (mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters /
replicate. LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.30
0.15
0.00Silver
(mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.30
0.15
0.00Silver
(mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
0.30
0.15
0.00
Site (distance from outfall)
Silver
(mg
/k
g)
LOR
LOR = 0.02 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.12 Concentrations of silver in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
500
250
0Zin
c (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
500
250
0Zin
c (
mg
/k
g)
LOR
2000m N
500m N B
500m N A100m N
Outfall BOutfall A
100m S500m S
2000m S
TIME ZERONSW BG
500
250
0
Site (distance from outfall)
Zin
c (
mg
/k
g)
LOR
MRL = 1000 (mg/kg) LOR = 0.01 (mg/kg)
January - April 2012
May - July 2012
March - May 2013
Figure 3.13 Concentrations of zinc in S. glomerata tissue (mg/kg, wet weight) following eight
weeks offshore deployment during January - April 2012, May - July 2012 and March - May 2013
(mean ± SE). For each site, N = 2 - 3 replicate samples with 10 composite oysters / replicate.
LOR = Limit of Reporting. Colours indicate different distances from the outfall.
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Table 3.1 Factorial GLM ANOVAs on metal/metalloids (mg/kg, wet weight) concentrations in
oyster tissue deployed during January - April 2012, May - July 2012 and March - May 2013.
N = 2 - 3 replicates (of a composite sample of 10 oysters) per site.
Arsenic Cadmium
Source DF MS F p MS F p
Time 2 0.05 2.96 0.09 0.08 19.67 0.00**
Site 7 0.02 1.15 0.39 0.00 0.45 0.85
Time * Site 13 0.02 3.36 0.00** 0.00 3.73 0.00**
Error 41 0.00 0.00
Transformation ln (x+1) n/a
Cobalt Copper
Source DF MS F pa MS F p
Time 2 0.00 16.00 0.00** 0.36 9.17 0.00**
Site 7 0.00 3.02 0.02* 0.09 2.15 0.11
Time * Site 13 0.00 3.15 0.00** 0.04 1.66 0.11
Error 41 0.00 0.02
Transformation n/a ln (x+1)
Iron Lead
Source DF MS F pa MS F p
a
Time 2 42.75 3.62 0.04* 0.00 30.53 0.00**
Site 7 35.41 3.00 0.01* 0.00 2.66 0.03*
Time * Site 13 34.68 2.94 0.00** 0.00 1.11 0.39
Error 41 11.81 0.00
Transformation n/a n/a
Manganese Nickel
Source DF MS F pa MS F p
a
Time 2 3.74 37.51 0.00** 0.01 8.53 0.00**
Site 7 0.36 3.58 0.00** 0.00 2.38 0.05
Time * Site 13 0.67 6.68 0.00** 0.00 1.74 0.10
Error 41 0.10 0.00
Transformation n/a n/a
a = randomization p-value, * = < 0.05, ** = < 0.01.
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Table 3.1 (continued) Factorial GLM ANOVAs on metal/metalloids (mg/kg, wet weight)
concentrations in oyster tissue deployed during January - April 2012, May - July 2012 and
March - May 2013. N = 2 - 3 replicates (of a composite sample of 10 oysters) per site.
Selenium Silver
Source DF MS F p MS F pa
Time 2 0.04 11.88 0.00** 0.01 3.62 0.03*
Site 7 0.01 3.05 0.04* 0.00 2.65 0.02**
Time * Site 13 0.00 1.47 0.17 0.00 2.58 0.02**
Error 41 0.00 0.00
Transformation ln (x+1) n/a
Zinc
Source DF MS F p
Time 2 96775.76 17.12 0.00**
Site 7 4949.69 0.88 0.55
Time * Site 13 5744.73 2.41 0.02*
Error 41 2386.59
Transformation n/a
a = randomization p-value, * = < 0.05, ** = < 0.01.
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Table 3.2 Regressions of oyster tissue metal/metalloids concentration with distance from the
outfall during each sampling event. N = 2 - 3 replicates (of a composite sample of ten oysters)
per site.
January - April 2012
Metals DF R2 F Standard p-value
Permutation T
Randomisation p-value Slope
Arsenic 1, 22 0.438 17.211 0.000**
+ve
Cadmium 1, 22 0.295 9.219 0.006**
-ve
Cobalt 1, 22 0.014 0.318 0.578 Copper 1, 22 0.002 0.0330 0.857 Iron 1, 22 0.126 3.0166 0.089 Lead 1, 22 0.157
-2.030 0.011* -ve
Manganese 1, 22 0.649 40.624 0.000**
+ve
Nickel 1, 22 0.041
-0.960 0.262 Selenium 1, 22 0.103 2.537 0.125
Silver 1, 22 0.100 2.468 0.130 Zinc 1, 22 0.148 3.851 0.062
May - July 2012
Arsenic 1,23 0.136 3.609 0.070 Cadmium 1,23 0.156
2.060 0.033* +ve
Cobalt 1,23 0.027 0.629 0.436 Copper 1,23 0.017 0.403 0.531 Iron 1,23 0.003 0.701 0.793
-ve
Lead 1,23 0.012 0.283 0.599 Manganese 1,23 0.046 1.104 0.304 Nickel 1,23 0.016 0.377 0.545 Selenium 1,23 0.111 2.867 0.104 Silver 1,23 0.028 0.665 0.423 Zinc 1,23 0.038 0.918 0.348
March - May 2013
Arsenic 1,13 0.112
-1.281 0.262 Cadmium 1,13 0.298 5.532 0.035*
+ve
Cobalt 1,13 0.010 0.137 0.717 Copper 1,13 0.006 0.076 0.786 Iron 1,13 0.289 5.297 0.038*
-ve
Lead 1,13 0.014
-0.432 1.000 Manganese 1,13 0.200
-1.810 0.031* -ve
Nickel 1,13 0.065 0.904 0.358 Selenium 1,13 0.062 0.869 0.368 Silver 1,13 0.041 0.562 0.467 Zinc 1,13 0.009 0.118 0.737
*= < 0.05, **= < 0.01
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3.4 Multivariate Analysis of Metal Profiles
3.4.1 January - April 2012
A non-metric MDS plot was generated in PRIMER 6 to compare similarities of metal/metalloid profiles
among sites for the January - April 2012 oyster deployment. Time zero samples were also included
in this analysis to determine how the multivariate metal profile changed post deployment. Chromium
and mercury were excluded due to all values being less than the LOR. The MDS plot is presented in
Figure 3.14.
The plot indicates that there is a weak gradient with distance from the outfall. The outfall sites and, to
a lesser extent 100 m sites, are clustered together although within site variability is high as samples
are not closely clustered. The time zero samples are however, quite segregated from the post-
deployment samples. There is little difference between the 500 and 2,000 m sites with overlapping of
these samples. Vectors on the plot suggest that higher concentrations of cadmium, cobalt, copper,
iron, manganese and zinc in two 100 m replicates (located to the left of the MDS plot) are driving the
separation of these samples on the plot.
Transform: Square root
Resemblance: D1 Euclidean distance
DistanceTimeZero
Outfall
100
500
2000
TimeZeroTimeZero
TimeZero
Outfall
OutfallOutfallOutfall
Outfall
Outfall North
North
North
South
South
South North
NorthNorth
South South
South North
North
North
South
South
South
Cadmium
Cobalt
Copper
Iron
Manganese
Silver
Zinc
2D Stress: 0.02
Figure 3.14 MDS plot of multivariate suite of metals/metalloids for each sample from the
January – April 2012 deployment. Symbols indicate the direction of each sample. N = 3
replicates (of a composite sample of 10 oysters) per site.
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3.4.2 May - July 2012
The MDS plot for May - July 2012 is presented in Figure 3.15. Time zero samples were also included
in this analysis to determine how the multivariate metal profile changed post deployment. Chromium
and mercury were excluded due to all values being less than the LOR. One sample taken at time
zero is clustered separately from all other samples showing that this sample had a different metal
profile. Vectors on the plot suggest that cadmium, copper, cobalt, iron, lead, nickel, manganese,
silver and zinc are responsible for this separation. The plot shows that there is little difference
between the metal profiles of sites with overlapping of most samples / distances.
Transform: Square root
Resemblance: D1 Euclidean distance
DistanceTimeZero
Outfall
100
500
2000
TimeZero
TimeZero
TimeZero
Outfall
OutfallOutfall
Outfall Outfall
Outfall
SouthSouthSouth
North
NorthNorth
North
NorthNorthNorthNorth
North
South
South
South
North
NorthSouth
South
Cadmium
Cobalt
Copper
Iron
Lead
Manganese
Nickel
Selenium
SilverZinc
2D Stress: 0.01
Figure 3.15 MDS plot of multivariate suite of metals/metalloids for each sample from the May -
July 2012 deployment. Symbols indicate the direction of each sample. N = 2 - 3 replicates (of a
composite sample of 10 oysters) per site.
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3.4.3 March - May 2013
The MDS plot for March - May 2013 is presented in Figure 3.16. Time zero samples were also
included in this analysis to determine how the multivariate metal profile changed post deployment.
Chromium and mercury were excluded due to all values being less than the LOR. Time zero samples
and two samples from the outfall are clustered separately from all other samples. Vectors on the plot
suggest that the metals arsenic, cadmium, copper, cobalt, iron, selenium and zinc are responsible for
this separation. No strong gradient of impact with distance from the outfall can be detected here.
Transform: Square root
Resemblance: D1 Euclidean distance
DistanceTimeZero
Outfall
100
500
2000
TimeZero
TimeZeroTimeZero
OutfallOutfall
OutfallOutfall
North
NorthNorth
SouthSouthNorth
North
South
SouthNorth North
Arsenic
Cadmium
Cobalt
Copper
Iron Nickel
Selenium
Zinc
2D Stress: 0.01
Figure 3.16 MDS plot of multivariate suite of metals/metalloids for each sample from the March
- May 2013 deployment. Symbols indicate the direction of each sample. N = 2 - 3 replicates (of
a composite sample of 10 oysters) per site.
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3.4.4 Overall
MDS plots were generated to compare metal/metalloids profiles over the three deployment periods to
determine overall patterns in the results. These are provided in Figures 3.17 - 3.19. The overall
MDS plots do not show any distinct patterns between distances or direction from the outfall. The
MDS plot by deployment periods shows that March - May 2013 was different and clustered separately
from January - April 2012 and May - July 2012. The vectors suggest that this was due to
concentrations of copper, cobalt, iron and zinc.
A PERMANOVA was undertaken in PRIMER 6 to determine if there were significant differences
among time or site in the suite of metals tested (Table 3.3). The analysis found that there was a
significant interaction between time and site suggesting that the patterns were inconsistent across
deployment periods (which reflects the univariate ANOVAs on individual metals as many also found
an interaction between time and site).
During January - April 2012, there were a number of differences in the suite of metals/metalloids
between sites. The 500 N site was different to Outfall A, 500 S and 2000 N. The 100 S site was also
different to Outfall A and 2000 N. In May - July 2012, the 500 S was different to 2000 N and Outfall A.
Following March - May 2013, the Outfall B site was different to 100 N and 500 S.
Table 3.3 PERMANOVA analysis of a suite of metals/metalloids in the S. glomerata tissue
following three deployment periods.
Factor DF MS Pseudo F Ratio p-value Permutations
Time 2 64.901 13.581 0.001** 999
Site 7 4.518 2.315 0.046* 999
Time * Site 13 4.857 2.489 0.007** 998
Error 41 1.952
* = <0.05, ** = < 0.01.
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Transform: Square root
Resemblance: D1 Euclidean distance
DistanceOutfall
100
500
2000
Cobalt
Copper
Iron
Zinc
2D Stress: 0.03
Figure 3.17 MDS plot of multivariate suite of metals/metalloids by distance from the outfall,
pooled over deployment period. N = 3 replicates (of a composite sample of ten oysters) per
site.
Transform: Square root
Resemblance: D1 Euclidean distance
TimeJanuary- April 2012
May- July 2012
March- May 2013
Cobalt
Copper
Iron
Zinc
2D Stress: 0.03
Figure 3.18 MDS plot of multivariate suite of metals/metalloids by deployment period, pooled
over distance from the outfall. N = 3 replicates (of a composite sample of ten oysters) per site.
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Transform: Square root
Resemblance: D1 Euclidean distance
DirectionOutfall
North
South
Cobalt
Copper
Iron
Zinc
2D Stress: 0.03
Figure 3.19 MDS plot of multivariate suite of metals/metalloids by direction from the outfall,
pooled over deployment period. N = 3 replicates (of a composite sample of ten oysters) per
site.
3.5 Power Analysis
A power analysis was carried out on the January - April 2012 data to estimate which sample sizes
would be required to detect a significant difference between sites for all metals/metalloids. A Type I
error rate of 5% (0.05) was used and a Type II error rate of 20% (0.2, power 80%) was considered
acceptable and a 50% effect size was used.
The power analysis estimated the amount of replication required to detect a significant difference
(p < 0.05) with a 50% effect size (Appendix 1) and is presented in Table 3.4. The estimate of
required sample size was three replicates per site for most metals. The low estimate of sample size
is likely due to the fact that replicate samples were a composite of ten oysters, reducing the variability.
Copper and cobalt had an estimate of four replicates. Nickel had an estimate of twelve replicates,
which was higher due to the higher variation between samples.
Overall, the variability within sites in oyster metal concentrations was low and the adopted sampling
size of three replicates (of a composite sample of ten oysters) per site should be sufficient to detect
differences in most metal concentrations with the exception of cobalt, copper and nickel.
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Table 3.4 Estimates of sample sizes required to detect a significant difference between
metal/metalloids in oysters based on power analysis of January - April 2012 sampling data.
Metal/Metalloid Sample Size Estimate
Arsenic 3
Inorganic Arsenic n/e
Cadmium 4
Chromium n/e
Cobalt 3
Copper 4
Iron 3
Lead n/e
Manganese 3
Mercury n/e
Nickel 12
Selenium 3
Silver 3
zinc 3
n/e = not estimable due to no variation between samples (all or majority were less than the LOR).
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4 DISCUSSION
The Burwood Beach Oyster Biomonitoring Study was undertaken to assess the potential for effluent
and biosolids discharges to lead to bioaccumulation of chemicals, over a range of spatial scales,
using Sydney rock oysters, S. glomerata, as a biomonitor. A specific requirement of the study was to
establish the zone in which there is a detectable increase in the concentration of chemicals in oysters
that is related to the outfall. Concentrations of a suite of organic and metal/metalloid chemicals were
measured in oyster tissue following four deployments of eight weeks in the receiving waters of the
Burwood Beach WWTW.
Concentrations of organics and metals/metalloids in oysters were compared to the ANZFA MRLs
(ANZFA 2011). These were used as a guide only (in the absence of other available guidelines) rather
than for assessing health risks for oyster consumption, as there are no commercially grown oysters
within the boundaries of this study.
4.1 Organics
Organic chemical levels in S. glomerata tissue were consistently lower than available ANZFA Food
Standard MRLs for Molluscs (ANZFA 2011). For the majority of measurements, organic chemicals
were lower than the LOR, but there were some exceptions.
In assessment of a suite of OC and OP pesticides, there were four detections of heptachlor, trans-
chlordane, cis-chlordane and dieldrin at Outfall B during January - April 2012. As they were detected
very close to the outfall, it is likely that the source of OC contamination is likely to be Burwood Beach
WWTW. The concentrations were lower than the ANZFA MRLs (2011). These pesticides have
sometimes been detected in routine analysis of effluent and biosolids which has been undertaken by
Hunter Water during 2006 – 2013, but at low concentrations. In effluent, mean concentrations of <
0.005 µg/L for heptachlor, 0.001 µg/L for chlordane and 0.000 for dieldrin have been measured. In
biosolids, mean concentrations of 0.006 µg/L have been measured for dieldrin (heptachlor and
chlordane have not been measured in biosolids). Previous measurements of organic chemicals in
oysters deployed in the receiving waters of Burwood Beach WWTW have not detected any OC or OP
pesticides (Ajani et al. 1999; NSW EPA 1996, reviewed in further detail in the introduction). During
January - April 2012, cis-chlordane was also detected in oysters from 2000 S. This site is located
near Redhead. The study of NSW EPA 1996; Ajani et al. 1999 also used Redhead as a reference
location and DDD was the only organic chemical that exceeded the LOR of 0.02 mg/kg.
Concentrations of PCB congeners and total PCB concentrations were lower than the LOR following
all deployments. No PCBs congeners were detected following all deployments (i.e. in January - April
2012, May- July 2012 and March - May 2013). This is similar to the findings of Ajani et al. 1999 and
NSW EPA 1996, who did not detect PCBs in oysters using the same LOR of 0.01 mg/kg.
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4.2 Metals
Assessment of metal/metalloid concentrations in S. glomerata tissue demonstrated that most metals
were at low concentrations. No metals/metalloids were found to exceed the available ANZFA MRLs
(ANZFA 2011). There were no consistent significant differences in the spatial patterns of
metals/metalloids to suggest that oysters deployed closer to the Burwood Beach WWTW had
accumulated higher concentrations of metals/metalloids than those located further away from the
outfall.
Concentrations of total arsenic in oysters exceeded 1 mg/kg during all sampling events. There is no
ANZFA MRL for total arsenic but the limit for inorganic arsenic is 1 mg/kg. Inorganic arsenic is the
portion of total arsenic that is inorganic and includes the most toxic forms, arsenite (As3+
) and
arsenate (As5+
) which have the capacity to inhibit enzymes and disrupt metabolic activities in marine
invertebrates (Cox 1995). All samples that exceeded 1 mg/kg for total arsenic were tested to
determine the proportion of inorganic arsenic and were all below the LOR of 0.05 mg/kg.
The majority of metals and metalloids in S. glomerata during this study were lower or at similar
concentrations to those that were reported by Scanes and Roach (1999). The exception was
selenium which was higher in most samples in comparison to the background level reported by
Scanes and Roach (1999). This was also reported by Andrew-Priestley (2011), who similarly
deployed S. glomerata in the receiving waters of Burwood Beach WWTW and at reference locations,
Redhead and Fingal Island (described in further detail in introduction). It was found that oysters at all
locations had higher levels of selenium in comparison to those reported by Scanes and Roach (1999).
There are likely to be differences between background metal concentrations between oysters in
estuarine locations and offshore environments but it does provide a point of comparison in the
absence of studies on oysters grown offshore. In general concentrations of metals and metalloids in
oysters living in NW estuaries would be expected to have higher concentrations as higher levels are
found in sediments of NSW estuaries in comparison to the continental shelf; Birch 2000).
Background levels of metals and metalloids may have also been higher during the 1990‟s in
comparison to the present day due to differences in environmental management.
Some metals were found to significantly decrease (p < 0.05, linear regression) with distance from the
outfall during one or two sampling events including cadmium during January - April 2012, iron during
May - July 2012 and March - May 2013 and manganese during March - May 2013. This result could
indicate that Burwood Beach WWTW is an occasional source of these metals into the marine
environment but as this result was not consistent across all sampling events this assumption should
be viewed with caution. Cadmium and manganese have been measured in the final treated effluent
and biosolids from Burwood Beach WWTW during 2006 - 2013 with higher concentrations detected in
the biosolids. Cadmium has been measured in biosolids at concentrations 0.5 - 128 µg/L with an
average of 5.93 µg/L while manganese has been measured in biosolids at concentrations 33 -
1270 µg/L with an average of 360 µg/L (N = 152; Hunter Water 2013).
Measurements of nickel in oysters may suggest an occasional impact. During January - April 2012,
nickel was elevated at 100 m N in comparison to the other sites, this pattern was not seen during the
following two deployment periods. This result could indicate that Burwood Beach WWTW is an
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occasional source of nickel in the marine environment close to the diffuser but again this result was
not consistent across sampling events so should be viewed with caution. Nickel has been measured
in biosolids from Burwood Beach WWTW, from 2006 - 2013, at concentrations 30 - 180 µg/L, with an
average of 47.21 µg/L (N = 152; Hunter Water 2013). Nickel is mainly used as alloys in an extensive
range of everyday domestic and industrial uses including building materials, batteries, mobile phones,
medical equipment, transport and power generation.
Oysters were tested for metals/metalloids prior to each deployment and most metals/metalloids were
found to increase following deployments in Burwood Beach WWTW receiving waters, including
arsenic, cadmium, copper, lead, mercury, nickel, selenium, silver and zinc. Increases in
metal/metalloid concentrations relative to time zero samples do not appear to be related to the outfall
as there were no patterns between elevated concentrations and sites or distance from the outfall.
This suggests that background concentrations of metals/metalloids are higher in the offshore waters
off Newcastle. The oysters deployed were depurated in clean waters for two weeks prior to
deployments (which may have reduced the concentrations of metals and metalloids). However, the
concentrations of metals/metalloids in oysters measured in this study are higher in comparison to
those measured in the concurrent study (with the same design) undertaken at Boulder Bay. Higher
concentrations in oysters deployed in Newcastle waters, in comparison to time zero oysters, may be
due to proximity to the Port of Newcastle which includes three coal export terminals and the historic
industrial background of the city which included a major steelworks (BHP).
Concentrations of mercury, selenium and zinc were higher in oysters deployed in March - May 2013.
For selenium, this was likely because concentrations in the time zero oysters were also higher relative
to the time zero oysters that were sampled in January - April 2012 and May - July 2012. For mercury
and zinc, it is unknown why there were temporal differences. Seasonal environmental changes such
as salinity, temperature and other water quality changes, as well as differences in the reproductive
status, weight and health of oysters can all affect the bioaccumulation of metals in oysters (Phillips
1980). Ajani et al. (1999) and NSW EPA (1996) also found differences between metal/metalloid
concentrations between deployments; concentrations were higher in oysters collected in August
1992, in comparison to February deployments in 1992 - 1996 and respective August deployments in
1993 - 1996.
The findings of this study show that overall metal/metalloids concentrations in oysters following
deployments were low and there was no evidence to suggest an impact from the Burwood Beach
WWTW. There are two possible scenarios for these findings:
1. The first scenario is that metal concentrations were not elevated in Burwood Beach WWTW
receiving waters and the WWTW was not a significant source during the deployments. Hence no
significant differences could be detected in the temporal patterns of metals and metalloids.
2. The second scenario is that the deployment period of eight weeks was not sufficient for S.
glomerata to equilibrate some of the metals/metalloids within their tissue. The rates of uptake
and equilibration in oysters has not been studied extensively or established for all metals,
however eight weeks exposure has been demonstrated as sufficient time of laboratory exposure
of non-essential metalloid/metals to accumulate to concentrations which are significantly different
from controls (Watling 1983; Boisson et al. 2003; Spooner et al. 2003) or to equilibrate (i.e. reach
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a plateau) in tissue (Scanes and Roach 1999). A longer exposure time may be required for
essential metals, such as, zinc and copper, as while oysters have been demonstrated to
bioaccumulate essential metals (George et al. 1978; Phillips and Yim 1981; Brown and
McPherson 1992; Phillips and Rainbow 1993; Phillips 1995; Spooner et al. 2003), it has been
suggested that molluscs may exhibit a degree of homeostasis for these metals depending on the
exposure concentration. Essential metals have a minimum metabolic requirement and as
suggested by Langston et al. 1998 (pg. 233) “copper concentrations may be buffered according to
the requirements for the copper containing pigment, haemocyanin”.
Importantly, no metals/metalloids consistently exhibited differences among sites or with distance from
the outfall. The multivariate profiles also suggest that there are no differences in the suite of metals
between sites.
It would be expected that with increases in future discharges of effluent and biosolids at Burwood
Beach WWTW that higher concentrations of organic chemicals and metal/metalloids would be found
via oyster biomonitoring studies.
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5 CONCLUSIONS
The Burwood Beach Oyster Biomonitoring Study was undertaken to assess the potential for effluent
and biosolids discharges to lead to bioaccumulation of chemicals, over a range of spatial scales,
using Sydney rock oysters, S. glomerata, as a biomonitor. A specific requirement of the study was to
establish the zone in which there is a detectable increase in the concentration of chemicals in oysters
that is related to the outfall. Concentrations of a suite of organic and metal/metalloid chemicals were
measured in oyster tissue following four deployments of eight weeks in the receiving waters of the
Burwood Beach WWTW.
Concentrations of organics and metals/metalloids in oysters were compared to the ANZFA MRLs
(ANZFA 2011). These were used as a guide only (in the absence of other available guidelines) rather
than for assessing health risks for oyster consumption, as there are no commercially grown oysters
within the boundaries of this study.
Organic chemical levels in oyster tissue at all sites, including the outfall site, were consistently
lower than available ANZFA Food Standard MRLs for Molluscs (ANZFA 2011). For the May -
July 2012 and the March - May 2013 deployments, all OCs, OPs, PCB congeners and total PCBs
were lower than the LOR (0.01 mg/kg). As the majority of organics were below the LOR,
statistical comparisons were not carried out. However in the January - April 2012 deployment,
some OC pesticides (i.e. heptachlor, trans-chlordane, cis-chlordane and dieldrin) were detected,
which does indicate their presence in the environment. The Burwood Beach WWTW discharge is
likely to be a source of these chemicals and should be continued to be monitored.
Most metals were at low concentrations in oysters following deployment. No metals/metalloids
were found to exceed the available ANZFA MRLs (ANZFA 2011). There were no consistent
significant differences in the spatial patterns of metals/metalloids to suggest that oysters deployed
closer to the Burwood Beach WWTW had accumulated higher concentrations of
metals/metalloids.
Oysters were tested for metals/metalloids prior to each deployment and most metals/metalloids
were found to increase following deployments in Burwood Beach WWTW receiving waters,
including arsenic, cadmium, copper, lead, mercury, nickel, selenium, silver and zinc. Increases in
metal/metalloid concentrations relative to time zero samples do not appear to be related to the
outfall as there were no patterns between elevated concentrations and sites or distance from the
outfall.
Most metal/metalloid concentrations were lower than or similar to those reported by Scanes and
Roach (1999) for oysters from NSW background estuarine locations. Concentrations of copper,
selenium and zinc were higher across most sites and of a similar magnitude spatially.
It would be expected that with increases in future discharges of effluent and biosolids at Burwood
Beach WWTW that higher concentrations of organic chemicals and metal/metalloids would be
found via oyster biomonitoring studies.
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6 ACKNOWLEDGEMENTS
We would like to thank those that assisted with the design and implementation of this study.
Consulting Environmental Engineers, Hunter Water, NSW EPA, NSW Marine Parks and NSW DPI
Fisheries assisted with the design of the sampling program and methodology. XL Oysters (Lemon
Tree Passage) provided all the oysters for the study. McLennan‟s Dive Services undertook
deployment and retrieval of oyster moorings and oyster bags. The National Measurement Institute
undertook all laboratory analyses in oyster tissue. All surveys were undertaken under NSW Fisheries
Permit # P110051-1.2 and NSW Marine Parks Permit #2011/046.
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Appendix 1 – Organic Chemical Concentrations in Oysters
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Summary of average trace organic concentrations (wet weight, mg/kg) measured in oysters following eight weeks offshore deployment for each
deployment period. For each site, N = three replicate samples with 10 composite oysters / replicate. Missing sites are indicated.
January - April 2012
Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 3 n= 3 n= 3
Organochlorine (OC) Pesticides
HCB 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Heptachlor 0.05 0.01 <0.01 0.0086 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Heptachlor epoxide 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Aldrin 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
gamma-BHC (Lindane) 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
alpha-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
beta-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
delta-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
trans-Chlordane 0.05 0.01 <0.01 0.028 <0.01 <0.01 <0.01 n/a <0.01 <0.01 0.0085 <0.01
cis-Chlordane 0.05 0.01 <0.01 0.007 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Oxychlordane 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Dieldrin 0.1 0.01 <0.01 0.007 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
pp-DDE 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
pp-DDD 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
pp-DDT 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
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January - April 2012
Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 3 n= 3 n= 3
Endrin - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Endrin Aldehyde - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Endrin Ketone - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
alpha-Endosulfan - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
beta-Endosulfan - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Endosulfan Sulfate - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
Methoxychlor - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <0.01
PCB Congeners PCB # 8 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 18 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 28 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 44 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 52 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 66 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 77 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 101 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 105 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 118 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 126 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 128 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
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January - April 2012
Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 3 n= 3 n= 3
PCB # 138 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 153 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 169 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 170 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 180 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 187 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 195 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 206 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
PCB # 209 - 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
Total PCB's < 0.5 0.01 <10 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 <0.01 <10
Organophosphate (OP) Pesticides
Dichlorvos - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Demeton-S-Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Diazinon - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Dimethoate - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Chlorpyrifos - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Chlorpyrifos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Malathion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Fenthion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Ethion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
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Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 3 n= 3 n= 3
Fenitrothion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Chlorfenvinphos (E) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Chlorfenvinphos (Z) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Parathion (Ethyl) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Parathion Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Pirimiphos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Pirimiphos Ethyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Azinphos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
Azinphos Ethyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 <0.02 <0.02
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Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 2 n= 2 n= 3
Organochlorine (OC) Pesticides
HCB 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Heptachlor 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Heptachlor epoxide 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Aldrin 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
gamma-BHC (Lindane) 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
alpha-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
beta-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
delta-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
trans-Chlordane 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
cis-Chlordane 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Oxychlordane 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Dieldrin 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
pp-DDE 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
pp-DDD 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
pp-DDT 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Endrin - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Endrin Aldehyde - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Endrin Ketone - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
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Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 2 n= 2 n= 3
alpha-Endosulfan - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
beta-Endosulfan - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Endosulfan Sulfate - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
Methoxychlor - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01
PCB Congeners PCB # 8 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 18 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 28 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 44 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 52 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 66 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 77 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 101 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 105 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 118 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 126 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 128 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 138 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 153 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 169 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
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Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 2 n= 2 n= 3
PCB # 170 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 180 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 187 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 195 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 206 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
PCB # 209 - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
Total PCB's < 0.5 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <0.01 <10
Organophosphate (OP) Pesticides
Dichlorvos - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Demeton-S-Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Diazinon - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Dimethoate - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Chlorpyrifos - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Chlorpyrifos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Malathion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Fenthion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Ethion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Fenitrothion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Chlorfenvinphos (E) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Chlorfenvinphos (Z) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
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Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 3 n=3 n= 3 n= 3 n= 3 n= 0 n= 3 n= 2 n= 2 n= 3
Parathion (Ethyl) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Parathion Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Pirimiphos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Pirimiphos Ethyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Azinphos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
Azinphos Ethyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02 <0.02
HUNTER WATER
OYSTER BIOMONITORING STUDY
BURWOOD BEACH WWTW
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October - December 2012
Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 2 n=2 n= 3 n= 2 n= 3 n= 0 n= 2 n= 2 n= 0 n= 3
Organochlorine (OC) Pesticides
HCB 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Heptachlor 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Heptachlor epoxide 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Aldrin 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
gamma-BHC (Lindane) 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
alpha-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
beta-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
delta-BHC 0.01 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
trans-Chlordane 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
cis-Chlordane 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Oxychlordane 0.05 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Dieldrin 0.1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
pp-DDE 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
pp-DDD 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
pp-DDT 1 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Endrin - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Endrin Aldehyde - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Endrin Ketone - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
alpha-Endosulfan - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
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Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 2 n=2 n= 3 n= 2 n= 3 n= 0 n= 2 n= 2 n= 0 n= 3
beta-Endosulfan - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Endosulfan Sulfate - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
Methoxychlor - 0.01 <0.01 <0.01 <0.01 <0.01 <0.01 n/a <0.01 <0.01 n/a <0.01
PCB Congeners PCB # 8 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 18 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 28 - 0.002 <0.002 0.0016 <0.002 0.0018 0.0015 n/a 0.0013 <0.002 n/a <0.002
PCB # 44 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 52 - 0.002 <0.002 <0.002 0.00155 0.00155 0.00155 n/a 0.0014 <0.002 n/a <0.002
PCB # 66 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 77 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 101 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 105 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 118 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 126 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 128 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 138 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 153 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 169 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 170 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
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Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 2 n=2 n= 3 n= 2 n= 3 n= 0 n= 2 n= 2 n= 0 n= 3
PCB # 180 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 187 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 195 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 206 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
PCB # 209 - 0.002 <0.002 <0.002 <0.002 <0.002 <0.002 n/a <0.002 <0.002 n/a <0.002
Total PCB's < 0.5 0.002 <0.002 0.0016 <0.002 0.00285 0.002 n/a 0.0020 <0.002 n/a <0.002
Organophosphate (OP) Pesticides
Dichlorvos - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Demeton-S-Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Diazinon - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Dimethoate - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Chlorpyrifos - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Chlorpyrifos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Malathion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Fenthion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Ethion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Fenitrothion - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Chlorfenvinphos (E) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Chlorfenvinphos (Z) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Parathion (Ethyl) - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
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October - December 2012
Class
Chemical
Comparison Criteria Average concentration (mg/kg, wet weight) with Distance from Outfall
ANZFAa LOR Outfall Mixing Zone Mixing Zone Reference Time Zero
mg/kg mg/kg A B 100 N 100 S 500 N A 500 N B
500 S 2000 N 2000 S TIME ZERO
n= 2 n=2 n= 3 n= 2 n= 3 n= 0 n= 2 n= 2 n= 0 n= 3
Parathion Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Pirimiphos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Pirimiphos Ethyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Azinphos Methyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
Azinphos Ethyl - 0.02 <0.02 <0.02 <0.02 <0.02 <0.02 n/a <0.02 <0.02 n/a <0.02
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Appendix 2 – Metal/Metalloid Concentrations in Oysters
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Arsenic Inorganic As Cadmium Chromium Cobalt Copper Iron Lead
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
Time Zero (January- April 2012) Time Zero 1 0.76 0.14 <0.05 0.07 18 21 0.02
Time Zero (January- April 2012) Time Zero 2 0.91 0.13 <0.05 0.07 18 19 0.02
Time Zero (January- April 2012) Time Zero 3 0.86 0.14 <0.05 0.07 19 25 0.02
January- April 2012 Outfall A 1 0.85 0.42 <0.05 0.04 14 9.6 0.02
January- April 2012 Outfall A 2 0.68 0.28 <0.05 0.03 11 9.4 0.02
January- April 2012 Outfall A 3 0.84 0.32 <0.05 0.04 13 10 0.02
January- April 2012 Outfall B 1 0.74 0.28 <0.05 0.04 10 9.1 0.02
January- April 2012 Outfall B 2 0.63 0.31 0.08 0.03 14 9.5 0.02
January- April 2012 Outfall B 3 0.79 0.34 <0.05 0.04 20 13 0.03
January- April 2012 100 N 1 0.83 0.33 0.05 0.04 18 12 0.02
January- April 2012 100 N 2 0.68 0.29 <0.05 0.04 17 14 0.05
January- April 2012 100 N 3 0.63 0.33 <0.05 0.05 23 20 0.04
January- April 2012 100 S 1 0.84 0.37 <0.05 0.05 19 17 0.03
January- April 2012 100 S 2 0.95 0.3 0.06 0.05 18 21 0.03
January- April 2012 100 S 3 0.92 0.34 <0.05 0.06 24 22 0.04
January- April 2012 500 N 1 0.86 0.3 <0.05 0.04 17 18 0.03
January- April 2012 500 N 2 0.67 0.36 <0.05 0.06 24 26 0.03
January- April 2012 500 N 3 0.77 0.34 <0.05 0.06 18 28 0.03
January- April 2012 500 S 1 0.79 0.29 <0.05 0.04 17 15 0.02
January- April 2012 500 S 2 0.92 0.28 <0.05 0.04 13 14 0.03
January- April 2012 500 S 3 1.1 < 0.05 0.3 <0.05 0.05 17 18 0.02
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Arsenic Inorganic As Cadmium Chromium Cobalt Copper Iron Lead
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
January- April 2012 2000 N 1 1.1 < 0.05 0.27 <0.05 0.05 14 18 0.02
January- April 2012 2000 N 2 1.1 < 0.05 0.3 <0.05 0.05 14 16 0.02
January- April 2012 2000 N 3 0.95 0.24 <0.05 0.05 14 19 0.02
January- April 2012 2000 S 1 1.2 < 0.05 0.3 <0.05 0.04 22 23 0.02
January- April 2012 2001 S 2 0.91 0.28 <0.05 0.04 17 13 0.02
January- April 2012 2002 S 3 0.92 0.26 <0.05 0.04 15 19 0.02
Time Zero (May- July 2012) Time Zero 1 0.71 0.17 <0.05 0.07 20 26 0.03
Time Zero (May- July 2012) Time Zero 2 1.2 <0.05 0.08 <0.05 0.04 8 13 0.02
Time Zero (May- July 2012) Time Zero 3 1.5 <0.05 0.15 0.08 0.08 13 92 0.06
May- July 2012 Outfall A 1 0.73 0.18 <0.05 0.04 16 16 0.04
May- July 2012 Outfall A 2 0.72 0.16 <0.05 0.04 14 13 0.03
May- July 2012 Outfall A 3 0.63 0.14 <0.05 0.04 11 14 0.03
May- July 2012 Outfall B 1 0.78 0.18 <0.05 0.05 17 15 0.03
May- July 2012 Outfall B 2 0.76 0.19 <0.05 0.05 19 16 0.04
May- July 2012 Outfall B 3 1 0.21 0.05 0.06 21 30 0.06
May- July 2012 100 S 1 1.1 <0.05 0.22 <0.05 0.05 19 20 0.05
May- July 2012 100 S 2 0.75 0.17 <0.05 0.05 17 21 0.04
May- July 2012 100 S 3 0.8 0.17 0.07 0.04 16 19 0.04
May- July 2012 100 N 1 1.2 <0.05 0.27 <0.05 0.07 23 26 0.07
May- July 2012 100 N 2 1.1 <0.05 0.16 <0.05 0.05 16 18 0.04
May- July 2012 100 N 3 1.2 <0.05 0.24 <0.05 0.06 22 20 0.04
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Arsenic Inorganic As Cadmium Chromium Cobalt Copper Iron Lead
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
May- July 2012 500 N A 1 1.1 <0.05 0.18 0.06 0.04 13 16 0.04
May- July 2012 500 N A 2 1.1 <0.05 0.26 0.05 0.05 22 22 0.04
May- July 2012 500 N A 3 1.2 <0.05 0.21 <0.05 0.05 19 20 0.04
May- July 2012 500 N B 1 0.84 0.22 0.05 0.06 20 18 0.05
May- July 2012 500 N B 2 0.94 0.22 0.05 0.05 21 18 0.04
May- July 2012 500 N B 3 0.73 0.21 <0.05 0.05 21 14 0.03
May- July 2012 500 S 1 1.2 <0.05 0.21 0.06 0.06 20 24 0.06
May- July 2012 500 S 2 1 <0.05 0.19 <0.05 0.05 21 19 0.05
May- July 2012 500 S 3 1.5 <0.05 0.25 <0.05 0.06 20 23 0.05
May- July 2012 2000 N 1 0.93 0.18 0.09 0.04 13 14 0.03
May- July 2012 2000 N 2 1.2 <0.05 0.2 <0.05 0.05 15 17 0.04
May- July 2012 2000 S 1 1.1 <0.05 0.31 <0.05 0.07 26 24 0.06
May- July 2012 2001 S 2 0.82 0.25 <0.05 0.05 19 18 0.04
Time Zero (March- May 2013) Time Zero 1 0.68 0.16 <0.05 0.07 14 35 0.04
Time Zero (March- May 2013) Time Zero 2 0.68 0.16 <0.05 0.06 17 24 0.04
Time Zero (March- May 2013) Time Zero 3 0.72 0.2 <0.05 0.06 17 25 0.03
March- May 2013 Outfall A 1 1.2 <0.05 0.31 <0.05 0.06 27 20 0.03
March- May 2013 Outfall A 2 1.2 <0.05 0.29 <0.05 0.06 20 18 0.03
March- May 2013 Outfall B 1 0.77 0.24 <0.05 0.04 18 13 0.02
March- May 2013 Outfall B 2 0.73 0.26 <0.05 0.05 19 17 0.03
March- May 2013 100 N 1 1.2 <0.05 0.3 <0.05 0.06 25 19 0.03
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Arsenic Inorganic As Cadmium Chromium Cobalt Copper Iron Lead
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
March- May 2013 100 N 2 1.3 <0.05 0.41 <0.05 0.07 25 22 0.04
March- May 2013 100 N 3 0.9 0.34 <0.05 0.07 20 22 0.04
March- May 2013 100 S 1 1.2 <0.05 0.28 <0.05 0.06 21 17 0.03
March- May 2013 100 S 2 1.1 <0.05 0.31 <0.05 0.05 20 19 0.04
March- May 2013 500 N A 1 1.2 <0.05 0.28 <0.05 0.06 21 18 0.03
March- May 2013 500 N A 2 1.1 <0.05 0.29 <0.05 0.06 21 15 0.03
March- May 2013 500 S 1 1.2 <0.05 0.34 <0.05 0.06 26 19 0.03
March- May 2013 500 S 2 1 <0.05 0.36 <0.05 0.04 22 12 0.03
March- May 2013 2000 N 1 0.82 0.36 <0.05 0.06 24 14 0.03
March- May 2013 2000 N 2 0.91 0.4 <0.05 0.06 20 13 0.03
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Manganese Mercury Nickel Selenium Silver Zinc
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
Time Zero (August- September 2012) Time Zero 1 1.8 <0.01 0.12 0.32 0.18 270
Time Zero (August- September 2013) Time Zero 2 2.6 <0.01 0.1 0.32 0.17 270
Time Zero (August- September 2013) Time Zero 3 2.4 <0.01 0.11 0.35 0.17 300
August- September 2012 Outfall A 1 0.57 <0.01 0.11 0.35 0.21 300
August- September 2012 Outfall A 2 0.51 <0.01 0.1 0.24 0.18 310
August- September 2012 Outfall A 3 0.62 <0.01 0.1 0.33 0.24 370
August- September 2012 Outfall B 1 0.7 <0.01 0.1 0.28 0.18 330
August- September 2012 Outfall B 2 0.53 <0.01 0.1 0.23 0.18 350
August- September 2012 Outfall B 3 0.64 <0.01 0.11 0.41 0.25 410
August- September 2012 100 N 1 0.81 0.01 0.11 0.34 0.24 370
August- September 2012 100 N 2 0.8 0.01 0.4 0.55 0.26 330
August- September 2012 100 N 3 1 0.01 0.24 0.44 0.28 430
August- September 2012 100 S 1 1.1 <0.01 0.15 0.47 0.32 400
August- September 2012 100 S 2 1.6 <0.01 0.15 0.47 0.26 370
August- September 2012 100 S 3 1 <0.01 0.16 0.47 0.31 510
August- September 2012 500 N 1 1.6 0.01 0.09 0.5 0.27 360
August- September 2012 500 N 2 1.2 0.01 0.16 0.48 0.33 380
August- September 2012 500 N 3 1.7 0.01 0.14 0.4 0.29 380
August- September 2012 500 S 1 1.1 <0.01 0.09 0.43 0.2 320
August- September 2012 500 S 2 1.5 0.01 0.12 0.49 0.17 280
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Manganese Mercury Nickel Selenium Silver Zinc
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
August- September 2012 500 S 3 2.5 <0.01 0.13 0.6 0.19 350
August- September 2012 2000 N 1 2.7 <0.01 0.12 0.51 0.18 310
August- September 2012 2000 N 2 1.9 <0.01 0.13 0.45 0.21 340
August- September 2012 2000 N 3 2.4 <0.01 0.12 0.37 0.2 320
August- September 2012 2000 S 1 2.9 <0.01 0.12 0.51 0.28 380
August- September 2012 2001 S 2 1.8 <0.01 0.1 0.4 0.18 330
August- September 2012 2002 S 3 1.9 <0.01 0.1 0.5 0.16 250
Time Zero (May- July 2012) Time Zero 1 1 0.01 0.08 0.36 0.25 330
Time Zero (May- July 2012) Time Zero 2 3.6 <0.01 0.05 0.42 0.1 130
Time Zero (May- July 2012) Time Zero 3 5.1 <0.01 0.11 0.66 0.13 230
May- July 2012 Outfall A 1 0.51 <0.01 0.09 0.32 0.15 310
May- July 2012 Outfall A 2 0.37 <0.01 0.09 0.3 0.15 250
May- July 2012 Outfall A 3 0.3 <0.01 0.09 0.29 0.12 190
May- July 2012 Outfall B 1 0.39 <0.01 0.11 0.33 0.19 310
May- July 2012 Outfall B 2 0.4 <0.01 0.11 0.34 0.18 360
May- July 2012 Outfall B 3 0.91 <0.01 0.14 0.43 0.23 380
May- July 2012 100 S 1 0.41 <0.01 0.11 0.43 0.2 370
May- July 2012 100 S 2 0.44 <0.01 0.12 0.33 0.14 290
May- July 2012 100 S 3 0.4 <0.01 0.11 0.36 0.17 290
May- July 2012 100 N 1 0.83 <0.01 0.14 0.51 0.37 400
May- July 2012 100 N 2 0.87 <0.01 0.11 0.41 0.17 300
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Manganese Mercury Nickel Selenium Silver Zinc
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
May- July 2012 100 N 3 0.69 <0.01 0.1 0.46 0.25 390
May- July 2012 500 N A 1 0.84 <0.01 0.09 0.46 0.15 250
May- July 2012 500 N A 2 0.54 <0.01 0.12 0.42 0.2 410
May- July 2012 500 N A 3 0.41 <0.01 0.11 0.49 0.24 330
May- July 2012 500 N B 1 0.83 <0.01 0.18 0.34 0.21 350
May- July 2012 500 N B 2 0.36 <0.01 0.12 0.35 0.26 370
May- July 2012 500 N B 3 0.3 <0.01 0.11 0.33 0.22 340
May- July 2012 500 S 1 0.64 <0.01 0.13 0.46 0.25 330
May- July 2012 500 S 2 0.6 <0.01 0.1 0.42 0.21 390
May- July 2012 500 S 3 1.1 <0.01 0.11 0.58 0.23 410
May- July 2012 2000 N 1 0.52 <0.01 0.11 0.33 0.15 250
May- July 2012 2000 N 2 1 <0.01 0.08 0.44 0.17 280
May- July 2012 2000 S 1 0.41 <0.01 0.13 0.46 0.32 430
May- July 2012 2001 S 2 0.37 <0.01 0.1 0.38 0.22 350
Time Zero (March- May 2013) Time Zero 1 1.7 <0.01 0.1 0.4 0.17 290
Time Zero (March- May 2013) Time Zero 2 1.8 <0.01 0.09 0.47 0.17 300
Time Zero (March- May 2013) Time Zero 3 1.7 <0.01 0.09 0.45 0.14 330
March- May 2013 Outfall A 1 1.3 0.01 0.1 0.58 0.21 550
March- May 2013 Outfall A 2 2.2 <0.01 0.09 0.6 0.19 430
March- May 2013 Outfall B 1 0.71 <0.01 0.08 0.42 0.17 390
March- May 2013 Outfall B 2 0.44 <0.01 0.07 0.42 0.18 350
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Manganese Mercury Nickel Selenium Silver Zinc
NT2_46 NT2_56 NT2_46 NT2_46 NT2_46 NT2_46
Deployment Period Site and Rep mg/kg mg/kg mg/kg mg/kg mg/kg mg/kg
March- May 2013 100 S 1 0.93 0.01 0.09 0.53 0.25 510
March- May 2013 100 S 2 1.2 0.01 0.11 0.67 0.21 540
March- May 2013 100 S 3 0.89 0.01 0.09 0.46 0.19 450
March- May 2013 100 N 1 1.4 0.01 0.1 0.57 0.18 510
March- May 2013 100 N 2 0.94 <0.01 0.08 0.5 0.19 450
March- May 2013 500 N A 1 1.1 <0.01 0.09 0.52 0.2 450
March- May 2013 500 N A 2 1.2 <0.01 0.09 0.58 0.19 480
March- May 2013 500 S 1 0.66 0.01 0.1 0.63 0.26 590
March- May 2013 500 S 2 1.3 0.01 0.06 0.49 0.13 470
March- May 2013 2000 N 1 0.49 <0.01 0.08 0.46 0.23 450
March- May 2013 2000 N 2 0.55 0.01 0.08 0.47 0.2 490
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Appendix 3: Power Analysis
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Power analyses to determine the suitability of the sample size used in
sampling period 1.
Power Analysis determined that a sample size of 3 (based on 50% effect size using reference
distance) should be sufficient to detect a significant difference in for most metal concentrations among
sites. The exceptions were cobalt, copper and nickel (which had respective estimates of 4, 4 and 12).
Arsenic
0.50.40.30.20.10.0
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 0.11
# Lev els 2
A ssumptions
3
Size
Sample
Power Curve for One-way ANOVA
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Cadmium
0.140.120.100.080.060.040.020.00
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 0.03
# Lev els 2
A ssumptions
3
Size
Sample
Power Curve for One-way ANOVA
Cobalt
0.0250.0200.0150.0100.0050.000
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 0.008
# Lev els 2
A ssumptions
4
Size
Sample
Power Curve for One-way ANOVA
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Copper
1086420
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 2.84
# Lev els 2
A ssumptions
4
Size
Sample
Power Curve for One-way ANOVA
Iron
14121086420
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 2.9
# Lev els 2
A ssumptions
3
Size
Sample
Power Curve for One-way ANOVA
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Manganese
1.41.21.00.80.60.40.20.0
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 0.32
# Lev els 2
A ssumptions
3
Size
Sample
Power Curve for One-way ANOVA
Nickel
0.090.080.070.060.050.040.030.020.010.00
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 0.05
# Lev els 2
A ssumptions
12
Size
Sample
Power Curve for One-way ANOVA
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Selenium
0.250.200.150.100.050.00
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 0.03
# Lev els 2
A ssumptions
2
Size
Sample
Power Curve for One-way ANOVA
Silver
0.100.080.060.040.020.00
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 0.02
# Lev els 2
A ssumptions
3
Size
Sample
Power Curve for One-way ANOVA
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Zinc
200150100500
1.0
0.8
0.6
0.4
0.2
0.0
Maximum Difference
Po
we
r
A lpha 0.05
StDev 41.58
# Lev els 2
A ssumptions
3
Size
Sample
Power Curve for One-way ANOVA
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Appendix 4: NMI QA/QC Reports
Page 1 of 2
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTDNMI QA Report No: WORL23/120411 Sample Matrix: Biota
Analyte Method LOR Blank Sample DuplicatesSample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % % %Organics Section
OC Pesticides N12/09540 N12/009540HCB NR19 0.01 <0.01 <0.01 <0.01 - - -Heptachlor NR19 0.01 <0.01 <0.01 <0.01 - 124 115Heptachlor epoxide NR19 0.01 <0.01 <0.01 <0.01 - - -Aldrin NR19 0.01 <0.01 <0.01 <0.01 - 78 109gamma-BHC (Lindane) NR19 0.01 <0.01 <0.01 <0.01 - 77 115alpha-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -beta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -delta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -trans-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -cis-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -Oxychlordane NR19 0.01 <0.01 <0.01 <0.01 - - -Dieldrin NR19 0.01 <0.01 <0.01 <0.01 - 103 132pp-DDE NR19 0.01 <0.01 <0.01 <0.01 - 90 130pp-DDD NR19 0.01 <0.01 <0.01 <0.01 - 95 134pp-DDT NR19 0.01 <0.01 <0.01 <0.01 - 76 91Endrin NR19 0.01 <0.01 <0.01 <0.01 - 80 133Endrin Aldehyde NR19 0.01 <0.01 <0.01 <0.01 - - -Endrin Ketone NR19 0.01 <0.01 <0.01 <0.01 - - -alpha-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -beta-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -Endosulfan Sulfate NR19 0.01 <0.01 <0.01 <0.01 - - -Methoxychlor NR19 0.01 <0.01 <0.01 <0.01 - - -Surrogate : DF-DDE NR19 - - 97 78 22 89 131
OP Pesticides N12/009563 N12/009540Dichlorvos NR19 0.01 <0.01 <0.01 <0.01 - - -Demeton-S-Methy NR19 0.01 <0.01 <0.01 <0.01 - - -Diazinon NR19 0.01 <0.01 <0.01 <0.01 - 107 100Dimethoate NR19 0.01 <0.01 <0.01 <0.01 - - -Chlorpyrifos NR19 0.01 <0.01 <0.01 <0.01 - 100 85Chlorpyrifos Methy NR19 0.01 <0.01 <0.01 <0.01 - - -Malathion (Maldison NR19 0.01 <0.01 <0.01 <0.01 - - -Fenthion NR19 0.01 <0.01 <0.01 <0.01 - - -Ethion NR19 0.01 <0.01 <0.01 <0.01 - 70 132Fenitrothion NR19 0.01 <0.01 <0.01 <0.01 - - -Chlorfenvinphos (E) NR19 0.01 <0.01 <0.01 <0.01 - - -Chlorfenvinphos (Z) NR19 0.01 <0.01 <0.01 <0.01 - - -Parathion (Ethyl) NR19 0.01 <0.01 <0.01 <0.01 - 87 65Parathion Methy NR19 0.01 <0.01 <0.01 <0.01 - - -Pirimiphos Ethy NR19 0.01 <0.01 <0.01 <0.01 - - -Pirimiphos Methy NR19 0.01 <0.01 <0.01 <0.01 - - -Azinphos Methy NR19 0.01 <0.01 <0.01 <0.01 - - -Azinphos Ethyl NR19 0.01 <0.01 <0.01 <0.01 - - -Surrogate : TPP - - 127 137 7.6 93 84
Results expressed in percentage (%) or mg/kg wherever appropriateAcceptable Spike recovery is 50-150%Acceptable RPDs on spikes and duplicates is 40%RPD= Relative Percentage DifferenceThis report shall not be reproduced except in ful
Signed:Danny SleeOrganics Manager, NMI-Pymble
Date: 1/05/2012
Recoveries
Australian GovernmentNational Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 2 of 2
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTDNMI QA Report No: WORL23/120411 Sample Matrix: Biota
Analyte Method LOR Blank Sample DuplicatesSample Duplicate RPD LCS Matrix Spike
ug/kg ug/kg ug/kg ug/kg % % %Organics SectionPCB Congeners N12/009540 N12/009540
#8 NR_19 10 <10 <10 <10 - - -#18 NR_19 10 <10 <10 <10 - - -#28 NR_19 10 <10 <10 <10 - - -#44 NR_19 10 <10 <10 <10 - - -#52 NR_19 10 <10 <10 <10 - 66 139#66 NR_19 10 <10 <10 <10 - - -#77 NR_19 10 <10 <10 <10 - - -#101 NR_19 10 <10 <10 <10 - - -#105 NR_19 10 <10 <10 <10 - - -#118 NR_19 10 <10 <10 <10 - 78 125#126 NR_19 10 <10 <10 <10 - - -#128 NR_19 10 <10 <10 <10 - - -#138 NR_19 10 <10 <10 <10 - 81 135#153 NR_19 10 <10 <10 <10 - - -#169 NR_19 10 <10 <10 <10 - - -#170 NR_19 10 <10 <10 <10 - - -#180 NR_19 10 <10 <10 <10 - 82 134#187 NR_19 10 <10 <10 <10 - - -#195 NR_19 10 <10 <10 <10 - - -#206 NR_19 10 <10 <10 <10 - - -#209 NR_19 10 <10 <10 <10 - - -
Results expressed in percentage (%) or ug/kg wherever appropriateAcceptable Spike recovery is 50-150% (PCB)Acceptable RPDs on spikes and duplicates is 40%RPD= Relative Percentage Difference.This report shall not be reproduced except in full
Signed:Danny SleeOrganics Manager, NMI-Pymble
Date: 1/05/2012
Recoveries
Australian GovernmentNational Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 1 of 1
Client: WORLEYPARSONS SERVICES PTY LTD NMI QA Report No: WORL23/120926T1 Sample Matrix: OYSTER
Analyte Method LOR Blank DuplicatesSample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % %Inorganics Section N12/025858 N12/025858
Arsenic NT2.46 0.05 <0.05 1.5 1.5 0 105 100Cadmium NT2.46 0.01 <0.01 0.16 0.15 6.5 99 100Chromium NT2.46 0.05 <0.05 0.07 0.09 24 106 97Cobalt NT2.46 0.01 <0.01 0.08 0.08 0 96 100Copper NT2.46 0.01 <0.01 13 14 7.4 102 98Iron NT2.46 0.5 <0.5 88 96 8.7 103 101Lead NT2.46 0.01 <0.01 0.06 0.06 0 90 100Manganese NT2.46 0.01 <0.01 5.1 5.1 0 101 96Mercury NT2.46 0.01 <0.01 <0.01 <0.01 ND 102 110Nickel NT2.46 0.01 <0.01 0.12 0.1 18 78 96Selenium NT2.46 0.05 <0.05 0.66 0.66 0 108 95Silver NT2.46 0.02 <0.02 0.12 0.14 15 109 99Zinc NT2.46 0.01 <0.01 210 240 13 106 86 Filename = K:\Inorganics\Quality System\QA Reports\TE\QAR2012\Food and Misc\Legend:Acceptable recovery is 75-120%.Acceptable RPDs on duplicates is 44% at concentrations >5 times LOR. Greater RPD may be expected at <5 times LOR.LOR = Limit Of Reporting ND = Not DeterminedRPD = Relative Percent Difference NA = Not ApplicableLCS = Laboratory Control Sample.#: Spike level is less than 50% of the sample's concentration, hence the recovery data is not reliable.**: reference value not available
Comments:Results greater than ten times LOR have been rounded to two significant figures.This report shall not be reproduced except in full.
Signed:
Dr Michael WuInorganics Manager, NMI-North Ryde
Date: 5/10/2012
QUALITY ASSURANCE REPORT
Recoveries
Australian GovernmentNational Measurement Institute
105 Delhi Road, North Ryde, 2113. Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 1 of 1
QUALITY ASSURANCE REPORT
Client: WORLEY PARSONS SERVICES PTY LTDNMI QA Report No: WORL23/120926 Sample Matrix: Biota
Analyte Method LOR Blank Sample DuplicatesSample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % % %Organics Section
OC PesticidesHCB NR19 0.01 <0.01 NA NA NA - NAHeptachlor NR19 0.01 <0.01 NA NA NA 112 NAHeptachlor epoxide NR19 0.01 <0.01 NA NA NA - NAAldrin NR19 0.01 <0.01 NA NA NA 125 NAgamma-BHC (Lindane) NR19 0.01 <0.01 NA NA NA 101 NAalpha-BHC NR19 0.01 <0.01 NA NA NA - NAbeta-BHC NR19 0.01 <0.01 NA NA NA - NAdelta-BHC NR19 0.01 <0.01 NA NA NA - NAtrans-Chlordane NR19 0.01 <0.01 NA NA NA - NAcis-Chlordane NR19 0.01 <0.01 NA NA NA - NAOxychlordane NR19 0.01 <0.01 NA NA NA - NADieldrin NR19 0.01 <0.01 NA NA NA 127 NApp-DDE NR19 0.01 <0.01 NA NA NA 120 NApp-DDD NR19 0.01 <0.01 NA NA NA 118 NApp-DDT NR19 0.01 <0.01 NA NA NA 111 NAEndrin NR19 0.01 <0.01 NA NA NA 117 NAEndrin Aldehyde NR19 0.01 <0.01 NA NA NA - NAEndrin Ketone NR19 0.01 <0.01 NA NA NA - NAalpha-Endosulfan NR19 0.01 <0.01 NA NA NA - NAbeta-Endosulfan NR19 0.01 <0.01 NA NA NA - NAEndosulfan Sulfate NR19 0.01 <0.01 NA NA NA - NAMethoxychlor NR19 0.01 <0.01 NA NA NA - NASurrogate : DF-DDE NR19 - - NA NA NA 89 NA
OP PesticidesDichlorvos NR19 0.01 <0.01 NA NA NA - NADemeton-S-Methyl NR19 0.01 <0.01 NA NA NA - NADiazinon NR19 0.01 <0.01 NA NA NA 102 NADimethoate NR19 0.01 <0.01 NA NA NA - NAChlorpyrifos NR19 0.01 <0.01 NA NA NA 100 NAChlorpyrifos Methyl NR19 0.01 <0.01 NA NA NA - NAMalathion (Maldison) NR19 0.01 <0.01 NA NA NA - NAFenthion NR19 0.01 <0.01 NA NA NA - NAEthion NR19 0.01 <0.01 NA NA NA 112 NAFenitrothion NR19 0.01 <0.01 NA NA NA - NAChlorfenvinphos (E) NR19 0.01 <0.01 NA NA NA - NAChlorfenvinphos (Z) NR19 0.01 <0.01 NA NA NA - NAParathion (Ethyl) NR19 0.01 <0.01 NA NA NA 101 NAParathion Methyl NR19 0.01 <0.01 NA NA NA - NAPirimiphos Ethyl NR19 0.01 <0.01 NA NA NA - NAPirimiphos Methyl NR19 0.01 <0.01 NA NA NA - NAAzinphos Methyl NR19 0.01 <0.01 NA NA NA - NAAzinphos Ethyl NR19 0.01 <0.01 NA NA NA - NASurrogate : TPP - - NA NA NA 102 NA
Results expressed in percentage (%) or mg/kg wherever appropriate.Acceptable Spike recovery is 50-150%Acceptable RPDs on spikes and duplicates is 40%.RPD= Relative Percentage Difference.This report shall not be reproduced except in full.
Signed:Danny SleeOrganics Manager, NMI-North Ryde
Date: 10/10/2012
Recoveries
Australian GovernmentNational Measurement Institute
105 Delhi Road, North Ryde NSW 2113 Tel: +61 2 9449 0111 www.measurement.gov.au
National Measurement Institute
Page 1 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTDNMI QA Report No: WORL23/120727 Sample Matrix: Biota
Analyte Method LOR Blank Sample DuplicatesSample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % % %Organics Section
OC Pesticides N12/019846 N12/019846HCB NR19 0.01 <0.01 <0.01 <0.01 - - -Heptachlor NR19 0.01 <0.01 <0.01 <0.01 - 124 126Heptachlor epoxide NR19 0.01 <0.01 <0.01 <0.01 - - -Aldrin NR19 0.01 <0.01 <0.01 <0.01 - 98 101gamma-BHC (Lindane) NR19 0.01 <0.01 <0.01 <0.01 - 119 119alpha-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -beta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -delta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -trans-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -cis-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -Oxychlordane NR19 0.01 <0.01 <0.01 <0.01 - - -Dieldrin NR19 0.01 <0.01 <0.01 <0.01 - 121 121pp-DDE NR19 0.01 <0.01 <0.01 <0.01 - 105 104pp-DDD NR19 0.01 <0.01 <0.01 <0.01 - 123 112pp-DDT NR19 0.01 <0.01 <0.01 <0.01 - 124 134Endrin NR19 0.01 <0.01 <0.01 <0.01 - 120 116Endrin Aldehyde NR19 0.01 <0.01 <0.01 <0.01 - - -Endrin Ketone NR19 0.01 <0.01 <0.01 <0.01 - - -alpha-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -beta-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -Endosulfan Sulfate NR19 0.01 <0.01 <0.01 <0.01 - - -Methoxychlor NR19 0.01 <0.01 <0.01 <0.01 - - -Surrogate : DF-DDE NR19 - - 97 97 0.0 96 96
OP Pesticides N12/019846 N12/019846Dichlorvos NR19 0.01 <0.01 <0.02 <0.02 - - -Demeton-S-Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Diazinon NR19 0.01 <0.01 <0.02 <0.02 - 120 129Dimethoate NR19 0.01 <0.01 <0.02 <0.02 - - -Chlorpyrifos NR19 0.01 <0.01 <0.02 <0.02 - 111 120Chlorpyrifos Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Malathion (Maldison) NR19 0.01 <0.01 <0.02 <0.02 - - -Fenthion NR19 0.01 <0.01 <0.02 <0.02 - - -Ethion NR19 0.01 <0.01 <0.02 <0.02 - 125 129Fenitrothion NR19 0.01 <0.01 <0.02 <0.02 - - -Chlorfenvinphos (E) NR19 0.01 <0.01 <0.02 <0.02 - - -Chlorfenvinphos (Z) NR19 0.01 <0.01 <0.02 <0.02 - - -Parathion (Ethyl) NR19 0.01 <0.01 <0.02 <0.02 - 126 146Parathion Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Pirimiphos Ethyl NR19 0.01 <0.01 <0.02 <0.02 - - -Pirimiphos Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Azinphos Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Azinphos Ethyl NR19 0.01 <0.01 <0.02 <0.02 - - -Surrogate : TPP - - 62 56 10 56 100
Results expressed in percentage (%) or mg/kg wherever appropriate.Acceptable Spike recovery is 50-150%Acceptable RPDs on spikes and duplicates is 40%.RPD= Relative Percentage Difference.This report shall not be reproduced except in full.
Signed:Danny SleeOrganics Manager, NMI-Pymble
Date: 16/08/2012
Recoveries
Australian GovernmentNational Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 2 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTDNMI QA Report No: WORL23/120727 Sample Matrix: Biota
Analyte Method LOR Blank Sample DuplicatesSample Duplicate RPD LCS Matrix Spike
ug/kg ug/kg ug/kg ug/kg % % %Organics SectionPCB Congeners N12/019846 N12/019846
#8 NR_19 10 <10 <10 <10 - - -#18 NR_19 10 <10 <10 <10 - - -#28 NR_19 10 <10 <10 <10 - - -#44 NR_19 10 <10 <10 <10 - - -#52 NR_19 10 <10 <10 <10 - 96 108#66 NR_19 10 <10 <10 <10 - - -#77 NR_19 10 <10 <10 <10 - - -#101 NR_19 10 <10 <10 <10 - - -#105 NR_19 10 <10 <10 <10 - - -#118 NR_19 10 <10 <10 <10 - 84 84#126 NR_19 10 <10 <10 <10 - - -#128 NR_19 10 <10 <10 <10 - - -#138 NR_19 10 <10 <10 <10 - 88 83#153 NR_19 10 <10 <10 <10 - - -#169 NR_19 10 <10 <10 <10 - - -#170 NR_19 10 <10 <10 <10 - - -#180 NR_19 10 <10 <10 <10 - 79 78#187 NR_19 10 <10 <10 <10 - - -#195 NR_19 10 <10 <10 <10 - - -#206 NR_19 10 <10 <10 <10 - - -#209 NR_19 10 <10 <10 <10 - - -
Results expressed in percentage (%) or ug/kg wherever appropriateAcceptable Spike recovery is 50-150% (PCB)Acceptable RPDs on spikes and duplicates is 40%RPD= Relative Percentage Difference.This report shall not be reproduced except in full
Signed:Danny SleeOrganics Manager, NMI-Pymble
Date: 16/08/2012
Recoveries
Australian GovernmentNational Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 3 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTDNMI QA Report No: WORL23/120727 Sample Matrix: Biota
Analyte Method LOR Blank Sample DuplicatesSample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % % %Organics Section
OC Pesticides N12/019864 N12/019865HCB NR19 0.01 <0.01 <0.01 <0.01 - - -Heptachlor NR19 0.01 <0.01 <0.01 <0.01 - 124 118Heptachlor epoxide NR19 0.01 <0.01 <0.01 <0.01 - - -Aldrin NR19 0.01 <0.01 <0.01 <0.01 - 98 96gamma-BHC (Lindane) NR19 0.01 <0.01 <0.01 <0.01 - 119 106alpha-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -beta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -delta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -trans-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -cis-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -Oxychlordane NR19 0.01 <0.01 <0.01 <0.01 - - -Dieldrin NR19 0.01 <0.01 <0.01 <0.01 - 121 111pp-DDE NR19 0.01 <0.01 <0.01 <0.01 - 105 100pp-DDD NR19 0.01 <0.01 <0.01 <0.01 - 123 104pp-DDT NR19 0.01 <0.01 <0.01 <0.01 - 124 123Endrin NR19 0.01 <0.01 <0.01 <0.01 - 120 118Endrin Aldehyde NR19 0.01 <0.01 <0.01 <0.01 - - -Endrin Ketone NR19 0.01 <0.01 <0.01 <0.01 - - -alpha-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -beta-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -Endosulfan Sulfate NR19 0.01 <0.01 <0.01 <0.01 - - -Methoxychlor NR19 0.01 <0.01 <0.01 <0.01 - - -Surrogate : DF-DDE NR19 - - 99 122 21 96 89
OP Pesticides N12/019864 N12/019865Dichlorvos NR19 0.01 <0.01 <0.02 <0.02 - - -Demeton-S-Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Diazinon NR19 0.01 <0.01 <0.02 <0.02 - 120 119Dimethoate NR19 0.01 <0.01 <0.02 <0.02 - - -Chlorpyrifos NR19 0.01 <0.01 <0.02 <0.02 - 111 112Chlorpyrifos Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Malathion (Maldison) NR19 0.01 <0.01 <0.02 <0.02 - - -Fenthion NR19 0.01 <0.01 <0.02 <0.02 - - -Ethion NR19 0.01 <0.01 <0.02 <0.02 - 125 123Fenitrothion NR19 0.01 <0.01 <0.02 <0.02 - - -Chlorfenvinphos (E) NR19 0.01 <0.01 <0.02 <0.02 - - -Chlorfenvinphos (Z) NR19 0.01 <0.01 <0.02 <0.02 - - -Parathion (Ethyl) NR19 0.01 <0.01 <0.02 <0.02 - 126 135Parathion Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Pirimiphos Ethyl NR19 0.01 <0.01 <0.02 <0.02 - - -Pirimiphos Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Azinphos Methyl NR19 0.01 <0.01 <0.02 <0.02 - - -Azinphos Ethyl NR19 0.01 <0.01 <0.02 <0.02 - - -Surrogate : TPP - - 68 54 23 56 92
Results expressed in percentage (%) or mg/kg wherever appropriate.Acceptable Spike recovery is 50-150%Acceptable RPDs on spikes and duplicates is 40%.RPD= Relative Percentage Difference.This report shall not be reproduced except in full.
Signed:Danny SleeOrganics Manager, NMI-Pymble
Date: 16/08/2012
Recoveries
Australian GovernmentNational Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 4 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTDNMI QA Report No: WORL23/120727 Sample Matrix: Biota
Analyte Method LOR Blank Sample DuplicatesSample Duplicate RPD LCS Matrix Spike
ug/kg ug/kg ug/kg ug/kg % % %Organics SectionPCB Congeners N12/019864 N12/019865
#8 NR_19 10 <10 <10 <10 - - -#18 NR_19 10 <10 <10 <10 - - -#28 NR_19 10 <10 <10 <10 - - -#44 NR_19 10 <10 <10 <10 - - -#52 NR_19 10 <10 <10 <10 - 96 112#66 NR_19 10 <10 <10 <10 - - -#77 NR_19 10 <10 <10 <10 - - -#101 NR_19 10 <10 <10 <10 - - -#105 NR_19 10 <10 <10 <10 - - -#118 NR_19 10 <10 <10 <10 - 84 81#126 NR_19 10 <10 <10 <10 - - -#128 NR_19 10 <10 <10 <10 - - -#138 NR_19 10 <10 <10 <10 - 88 73#153 NR_19 10 <10 <10 <10 - - -#169 NR_19 10 <10 <10 <10 - - -#170 NR_19 10 <10 <10 <10 - - -#180 NR_19 10 <10 <10 <10 - 79 88#187 NR_19 10 <10 <10 <10 - - -#195 NR_19 10 <10 <10 <10 - - -#206 NR_19 10 <10 <10 <10 - - -#209 NR_19 10 <10 <10 <10 - - -
Results expressed in percentage (%) or ug/kg wherever appropriateAcceptable Spike recovery is 50-150% (PCB)Acceptable RPDs on spikes and duplicates is 40%RPD= Relative Percentage Difference.This report shall not be reproduced except in full
Signed:Danny SleeOrganics Manager, NMI-Pymble
Date: 16/08/2012
Recoveries
Australian GovernmentNational Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 1 of 1
Client: WORLEYPARSONS SERVICES PTY LTD NMI QA Report No: WORL23/120926T2 Sample Matrix: OYSTER
Analyte Method LOR Blank DuplicatesSample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % %Inorganics Section N12/025858 N12/025858
Arsenic inorganic NT2.56 0.05 <0.05 <0.05 <0.05 ND 98 100 Filename = K:\Inorganics\Quality System\QA Reports\TE\QAR2012\Food and Misc\Legend:Acceptable recovery is 75-120%.Acceptable RPDs on duplicates is 44% at concentrations >5 times LOR. Greater RPD may be expected at <5 times LOR.LOR = Limit Of Reporting ND = Not DeterminedRPD = Relative Percent Difference NA = Not ApplicableLCS = Laboratory Control Sample.#: Spike level is less than 50% of the sample's concentration, hence the recovery data is not reliable.**: reference value not available
Comments:Results greater than ten times LOR have been rounded to two significant figures.This report shall not be reproduced except in full.
Signed:
Dr Michael WuInorganics Manager, NMI-North Ryde
Date: 12/10/2012
QUALITY ASSURANCE REPORT
Recoveries
Australian GovernmentNational Measurement Institute
105 Delhi Road, North Ryde, 2113. Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 1 of 1
Client: WORLEYPARSONS SERVICES PTY LTD NMI QA Report No: WORL23/130531T1 Sample Matrix: SEAFOOD
WORL23/130531/1T1
Analyte Method LOR Blank DuplicatesSample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % %Inorganics Section N13/014643 N13/014643
Arsenic NT2.46 0.05 <0.05 1.7 1.7 0 97 99Arsenic Inorganic NT2.56 0.05 <0.05 <0.05 <0.05 ND 106 86Cadmium NT2.46 0.01 <0.01 0.35 0.37 5.6 96 100Chromium NT2.46 0.05 <0.05 <0.05 <0.05 ND 100 98Cobalt NT2.46 0.01 <0.01 0.06 0.06 5.1 96 100Copper NT2.46 0.01 <0.01 17 18 5.7 101 100Iron NT2.46 0.5 <0.5 26 26 0 89 96Lead NT2.46 0.01 <0.01 0.04 0.04 0 87 100Manganese NT2.46 0.01 <0.01 4.0 4.1 2.5 102 100Mercury NT2.46 0.01 <0.01 <0.01 <0.01 ND 101 99Nickel NT2.46 0.01 <0.01 0.10 0.10 0 92 100Selenium NT2.46 0.05 <0.05 0.68 0.74 8.5 101 100Silver NT2.46 0.02 <0.02 0.2 0.21 4.9 98 100Zinc NT2.46 0.01 <0.01 330 330 0 105 92
Filename = K:\Inorganics\Quality System\QA Reports\TE\QAR2013\Food & Misc\Legend:Acceptable recovery is 75-120%.Acceptable RPDs on duplicates is 44% at concentrations >5 times LOR. Greater RPD may be expected at <5 times LOR.LOR = Limit Of Reporting ND = Not DeterminedRPD = Relative Percent Difference NA = Not ApplicableLCS = Laboratory Control Sample.#: Spike level is less than 50% of the sample's concentration, hence the recovery data is not reliable.**: reference value not available
Comments:Results greater than ten times LOR have been rounded to two significant figures.This report shall not be reproduced except in full.
Signed:
Dr Michael WuInorganics Manager, NMI-North Ryde
Date: 20/06/2013
QUALITY ASSURANCE REPORT
Recoveries
Australian GovernmentNational Measurement Institute
105 Delhi Road, North Ryde, 2113. Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 1 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTD
NMI QA Report No: WORL23/130531 Sample Matrix: Biota
Analyte Method LOR Blank Sample Duplicates
Sample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % % %
Organics SectionOC Pesticides N13/014608 N13/014608
HCB NR19 0.01 <0.01 <0.01 <0.01 - - -
Heptachlor NR19 0.01 <0.01 <0.01 <0.01 - 91 103
Heptachlor epoxide NR19 0.01 <0.01 <0.01 <0.01 - - -
Aldrin NR19 0.01 <0.01 <0.01 <0.01 - 91 98
gamma-BHC (Lindane) NR19 0.01 <0.01 <0.01 <0.01 - 78 103
alpha-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -
beta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -
delta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -
trans-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -
cis-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -
Oxychlordane NR19 0.01 <0.01 <0.01 <0.01 - - -
Dieldrin NR19 0.01 <0.01 <0.01 <0.01 - 93 113
pp-DDE NR19 0.01 <0.01 <0.01 <0.01 - 83 79
pp-DDD NR19 0.01 <0.01 <0.01 <0.01 - 97 92
pp-DDT NR19 0.01 <0.01 <0.01 <0.01 - 74 62
Endrin NR19 0.01 <0.01 <0.01 <0.01 - 94 110
Endrin Aldehyde NR19 0.01 <0.01 <0.01 <0.01 - - -
Endrin Ketone NR19 0.01 <0.01 <0.01 <0.01 - - -
alpha-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -
beta-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -
Endosulfan Sulfate NR19 0.01 <0.01 <0.01 <0.01 - - -
Methoxychlor NR19 0.01 <0.01 <0.01 <0.01 - - -
Surrogate : DF-DDE NR19 - - 73 72 1.4 63 70
OP Pesticides N13/014608 N13/014608
Dichlorvos NR19 0.01 <0.01 <0.01 <0.01 - - -
Demeton-S-Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Diazinon NR19 0.01 <0.01 <0.01 <0.01 - 106 127
Dimethoate NR19 0.01 <0.01 <0.01 <0.01 - - -
Chlorpyrifos NR19 0.01 <0.01 <0.01 <0.01 - 117 124
Chlorpyrifos Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Malathion (Maldison) NR19 0.01 <0.01 <0.01 <0.01 - - -
Fenthion NR19 0.01 <0.01 <0.01 <0.01 - - -
Ethion NR19 0.01 <0.01 <0.01 <0.01 - 110 100
Fenitrothion NR19 0.01 <0.01 <0.01 <0.01 - - -
Chlorfenvinphos (E) NR19 0.01 <0.01 <0.01 <0.01 - - -
Chlorfenvinphos (Z) NR19 0.01 <0.01 <0.01 <0.01 - - -
Parathion (Ethyl) NR19 0.01 <0.01 <0.01 <0.01 - 116 112
Parathion Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Pirimiphos Ethyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Pirimiphos Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Azinphos Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Azinphos Ethyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Surrogate : TPP - - 95 96 1.0 57 89
Results expressed in percentage (%) or mg/kg wherever appropriate.Acceptable Spike recovery is 50-150%Acceptable RPDs on spikes and duplicates is 40%.
RPD= Relative Percentage Difference.
This report shall not be reproduced except in full.
Signed:Danny SleeOrganics Manager, NMI-North Ryde
Date: 26/06/2013
Recoveries
Australian Government
National Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 2 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTD
NMI QA Report No: WORL23/130531 Sample Matrix: Biota
Analyte Method LOR Blank Sample Duplicates
Sample Duplicate RPD LCS Matrix Spike
mg/kg mg/kg mg/kg mg/kg % % %
Organics SectionOC Pesticides N13/014618 N13/014618
HCB NR19 0.01 <0.01 <0.01 <0.01 - - -
Heptachlor NR19 0.01 <0.01 <0.01 <0.01 - 91 100
Heptachlor epoxide NR19 0.01 <0.01 <0.01 <0.01 - - -
Aldrin NR19 0.01 <0.01 <0.01 <0.01 - 91 92
gamma-BHC (Lindane) NR19 0.01 <0.01 <0.01 <0.01 - 78 103
alpha-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -
beta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -
delta-BHC NR19 0.01 <0.01 <0.01 <0.01 - - -
trans-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -
cis-Chlordane NR19 0.01 <0.01 <0.01 <0.01 - - -
Oxychlordane NR19 0.01 <0.01 <0.01 <0.01 - - -
Dieldrin NR19 0.01 <0.01 <0.01 <0.01 - 93 112
pp-DDE NR19 0.01 <0.01 <0.01 <0.01 - 83 80
pp-DDD NR19 0.01 <0.01 <0.01 <0.01 - 97 92
pp-DDT NR19 0.01 <0.01 <0.01 <0.01 - 74 62
Endrin NR19 0.01 <0.01 <0.01 <0.01 - 94 114
Endrin Aldehyde NR19 0.01 <0.01 <0.01 <0.01 - - -
Endrin Ketone NR19 0.01 <0.01 <0.01 <0.01 - - -
alpha-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -
beta-Endosulfan NR19 0.01 <0.01 <0.01 <0.01 - - -
Endosulfan Sulfate NR19 0.01 <0.01 <0.01 <0.01 - - -
Methoxychlor NR19 0.01 <0.01 <0.01 <0.01 - - -
Surrogate : DF-DDE NR19 - - 78 69 12 63 70
OP Pesticides N13/014618 N13/014618
Dichlorvos NR19 0.01 <0.01 <0.01 <0.01 - - -
Demeton-S-Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Diazinon NR19 0.01 <0.01 <0.01 <0.01 - 106 127
Dimethoate NR19 0.01 <0.01 <0.01 <0.01 - - -
Chlorpyrifos NR19 0.01 <0.01 <0.01 <0.01 - 117 119
Chlorpyrifos Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Malathion (Maldison) NR19 0.01 <0.01 <0.01 <0.01 - - -
Fenthion NR19 0.01 <0.01 <0.01 <0.01 - - -
Ethion NR19 0.01 <0.01 <0.01 <0.01 - 110 82
Fenitrothion NR19 0.01 <0.01 <0.01 <0.01 - - -
Chlorfenvinphos (E) NR19 0.01 <0.01 <0.01 <0.01 - - -
Chlorfenvinphos (Z) NR19 0.01 <0.01 <0.01 <0.01 - - -
Parathion (Ethyl) NR19 0.01 <0.01 <0.01 <0.01 - 116 115
Parathion Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Pirimiphos Ethyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Pirimiphos Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Azinphos Methyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Azinphos Ethyl NR19 0.01 <0.01 <0.01 <0.01 - - -
Surrogate : TPP - - 84 82 2.4 57 86
Results expressed in percentage (%) or mg/kg wherever appropriate.Acceptable Spike recovery is 50-150%Acceptable RPDs on spikes and duplicates is 40%.
RPD= Relative Percentage Difference.
This report shall not be reproduced except in full.
Signed:Danny SleeOrganics Manager, NMI-North Ryde
Date: 26/06/2013
Recoveries
Australian Government
National Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 3 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTD
NMI QA Report No: WORL23/130531 Sample Matrix: Biota
Analyte Method LOR Blank Sample Duplicates
Sample Duplicate RPD LCS Matrix Spike
ug/kg ug/kg ug/kg ug/kg % % %
Organics Section
PCB Congeners N13/014608 N13/014608
#8 NR_19 2 <2 <2 <2 - - -
#18 NR_19 2 <2 <2 <2 - - -
#28 NR_19 2 <2 <2 <2 - - -
#44 NR_19 2 <2 <2 <2 - - -
#52 NR_19 2 <2 <2 <2 - 89 117
#66 NR_19 2 <2 <2 <2 - - -
#77 NR_19 2 <2 <2 <2 - - -
#101 NR_19 2 <2 <2 <2 - - -
#105 NR_19 2 <2 <2 <2 - - -
#118 NR_19 2 <2 <2 <2 - 87 124
#126 NR_19 2 <2 <2 <2 - - -
#128 NR_19 2 <2 <2 <2 - - -
#138 NR_19 2 <2 <2 <2 - 99 115
#153 NR_19 2 <2 <2 <2 - - -
#169 NR_19 2 <2 <2 <2 - - -
#170 NR_19 2 <2 <2 <2 - - -
#180 NR_19 2 <2 <2 <2 - 93 115
#187 NR_19 2 <2 <2 <2 - - -
#195 NR_19 2 <2 <2 <2 - - -
#206 NR_19 2 <2 <2 <2 - - -
#209 NR_19 2 <2 <2 <2 - - -
Results expressed in percentage (%) or ug/kg wherever appropriate.
Acceptable Spike recovery is 50-150% (PCB)
Acceptable RPDs on spikes and duplicates is 40%.
RPD= Relative Percentage Difference.
This report shall not be reproduced except in full.Signed:
Danny SleeDate: Organics Manager, NMI-North Ryde
26/06/2013
Recoveries
Australian Government
National Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute
Page 4 of 4
QUALITY ASSURANCE REPORT
Client: WORLEYPARSONS SERVICES PTY LTD
NMI QA Report No: WORL23/130531 Sample Matrix: Biota
Analyte Method LOR Blank Sample Duplicates
Sample Duplicate RPD LCS Matrix Spike
ug/kg ug/kg ug/kg ug/kg % % %
Organics Section
PCB Congeners N13/014618 N13/014618
#8 NR_19 2 <2 <2 <2 - - -
#18 NR_19 2 <2 <2 <2 - - -
#28 NR_19 2 <2 <2 <2 - - -
#44 NR_19 2 <2 <2 <2 - - -
#52 NR_19 2 <2 <2 <2 - 89 94
#66 NR_19 2 <2 <2 <2 - - -
#77 NR_19 2 <2 <2 <2 - - -
#101 NR_19 2 <2 <2 <2 - - -
#105 NR_19 2 <2 <2 <2 - - -
#118 NR_19 2 <2 <2 <2 - 87 94
#126 NR_19 2 <2 <2 <2 - - -
#128 NR_19 2 <2 <2 <2 - - -
#138 NR_19 2 <2 <2 <2 - 99 117
#153 NR_19 2 <2 <2 <2 - - -
#169 NR_19 2 <2 <2 <2 - - -
#170 NR_19 2 <2 <2 <2 - - -
#180 NR_19 2 <2 <2 <2 - 93 107
#187 NR_19 2 <2 <2 <2 - - -
#195 NR_19 2 <2 <2 <2 - - -
#206 NR_19 2 <2 <2 <2 - - -
#209 NR_19 2 <2 <2 <2 - - -
Results expressed in percentage (%) or ug/kg wherever appropriate.
Acceptable Spike recovery is 50-150% (PCB)
Acceptable RPDs on spikes and duplicates is 40%.
RPD= Relative Percentage Difference.
This report shall not be reproduced except in full.Signed:
Danny SleeDate: Organics Manager, NMI-North Ryde
26/06/2013
Recoveries
Australian Government
National Measurement Institute
1 Suakin Street, Pymble NSW 2073 Tel: +61 2 9449 0111 Fax: +61 2 9449 1653 www.measurement.gov.au
National Measurement Institute