TC-3752
FINAL REPORT
EPA-910/9-85-134b
COMMENCEMENT BAY
NEARSHORE / TIDEFLATS
REMEDIAL INVESTIGATION
VOLUME ^
AUGUST, 1985
PREPARED FOR:
WASHINGTON STATE DEPARTMENT OF ECOLOGY
AND U.S. ENVIRONMENTAL PROTECTION AGENCY
Mr. James D. Kruli, Project Manager
Washington State Department of Ecology
Olympia, Washington
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TC-3752
Final Report
COMMENCEMENT BAY NEARSHORE/
TIDEFLATS REMEDIAL INVESTIGATION
Volume 1
by
Tetra Tech, Inc.
for
Washington State Department of Ecology
and U.S. Environmental Protection Agency
Mr. James D. KruTI, Project Manager
Washington State Department of Ecology
Olympia, Washington
August, 1985
Tetra Tech, Inc.
11820 Northup Way, Suite 100
Bellevue, Washington 98005
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CONTENTS
Page
LIST OF FIGURES ix
LIST OF TABLES xvi
ACKNOWLEDGEMENTS xxii
1.0 INTRODUCTION 1.1
1.1 BACKGROUND 1.1
1.2 SITE DESCRIPTION 1.1
1.3 NATURE AND EXTENT OF PROBLEM 1.4
1.4 COOPERATIVE AGREEMENT 1.6
1.5 REPORT OVERVIEW 1.7
2.0 METHODS 2.1
2.1 GENERAL APPROACH 2.1
2.1.1 Study Design 2.1
2.1.2 Station Locations 2.1
2.1.3 Data Analysis Methods 2.16
2.1.4 Geophysical Survey 2.18
2.2 SEDIMENT CHEMISTRY 2.18
2.2.1 Field Sampling 2.19
2.2.2 Laboratory Analysis for Metals 2.21
2.2.3 Laboratory Analysis for Organic Compounds 2.21
2.2.4 Ancillary Analyses 2.24
2.3 WATER COLUMN CHEMISTRY 2.25
2.3.1 Field Sampling 2.25
2.3.2 Laboratory Analysis 2.27
2.4 BENTHIC MACROINVERTEBRATES 2.28
2.4.1 Field Sampling 2.28
2.4.2 Laboratory Analysis 2.29
11
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2.5 SEDIMENT BIOASSAYS 2.29
2.5.1 Field Sampling 2.29
2.5.2 Laboratory Analysis 2.29
2.6 FISH HISTOPATHOLOGY 2.32
2.6.1 Field Sampling 2.32
2.6.2 Histopathological Examination 2.33
2.7 BIOACCUMULATION 2.33
2.7.1 Field Sampling 2.33
2.7.2 Laboratory Analysis for Metals 2.34
2.7.3 Laboratory Analysis for Organic Compounds 2.35
2.8 DATA MANAGEMENT 2.36
2.8.1 The Database 2.36
2.8.2 Data Analysis 2.37
2.8.3 Graphics 2.37
2.8.4 Quality Control 2.38
2.8.5 Library 2.38
2.9 HEALTH AND SAFETY 2.38
2.10 SAMPLING AND ANALYSIS QA/QC 2.39
2.10.1 Sample Collection 2.39
2.10.2 Organic Compound Analyses 2.40
2.10.3 Trace Metals and Ancillary Analyses 2.41
2.10.4 Benthic Macroinvertebrates, Sediment Bioassays,
and Fish Histopathology 2.41
2.11 RISK ASSESSMENT 2.41
2.11.1 Exposure Evaluation 2.44
2.11.2 Health Effects (Hazard Assessment) Methodology 2.47
2.11.3 Risk Assessment Calculations 2.47
2.12 SOURCE IDENTIFICATION 2.52
2.12.1 Sediment Chemistry 2.52
2.12.2 Water Quality Data 2.57
2.12.3 Point Sources and Runoff 2.57
2.12.4 Groundwater Sources 2.62
2.12.5 Atmospheric Sources 2.63
2.12.6 Spills 2.63
2.12.7 Dredging 2.64
iii
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3.0 RESULTS 3.1
3.1 SEDIMENT CHEMISTRY 3.1
3.1.1 Bulk Sediment Characteristics 3.1
3.1.2 Normalization of Chemical Concentrations 3.10
3.1.3 Sediment Metals 3.13
3.1.4 Sediment Organic Compounds 3.20
3.1.5 Prioritization of Areas Based on Sediment
Contamination 3.39
3.1.6 Comparison with Historical Conditions 3.69
3.1.7 Contamination of Waterway Suspended Solids 3.72
3.1.8 Summary 3.73
3.2 BENTHIC MACROINVERTEBRATES 3.78
3.2.1 Introduction 3.78
3.2.2 Characteristics of Benthic Communities in
Commencement Bay and Carr Inlet 3.78
3.2.3 Comparisons Among Study Areas 3.80
3.2.4 Comparisons Within Study Areas 3.92
3.2.5 Classification Analyses 3.98
3.2.6 Animal-Sediment Relationships 3.106
3.2.7 Indices for Decision Criteria 3.117
3.2.8 Comparisons With Past Studies 3.121
3.2.9 Summary 3.122
3.3 SEDIMENT TOXICITY 3.123
3.3.1 Introduction 3.123
3.3.2 Amphipod Sediment Bioassays 3.125
3.3.3 Oyster Larvae Sediment Bioassays 3.125
3.3.4 Discussion 3.133
3.3.5 Comparison With Historical Data 3.134
3.3.6 Summary 3.140
3.4 FISH ECOLOGY 3.140
3.4.1 Introduction 3.140
3.4.2 Total Fish Assemblages 3.140
3.4.3 English Sole Populations 3.143
3.4.4 Summary 3.151
3.5 FISH HISTOPATHOLOGY 3.153
3.5.1 Introduction 3.153
3.5.2 External Abnormalities 3.153
3.5.3 Classification of Liver Conditions 3.153
3.5.4 Effects of Sex 3.155
3.5.5 Effects of Age 3.157
3.5.6 Spatial Patterns of Individual Disorders 3.157
3.5.7 Spatial Patterns of Fish Having One or More
Major Lesion 3.162
3.5.8 Fish Condition Comparisons 3.164
iv
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3.5.9 Comparisons With Historical Data 3.164
3.5.10 Summary 3.169
3.6 BIOACCUMULATION 3.170
3.6.1 Introduction 3.170
3.6.2 Metals in Fish Muscle 3.172
3.6.3 Metals in Crab Muscle 3.174
3.6.4 Organic Compounds in Fish Muscle 3.174
3.6.5 Organic Compounds in Crab Muscle 3.193
3.6.6 Comparison With Other Studies 3.195
3.6.7 Summary 3.200
4.0 CONTAMINANT, TOXICITY, AND BIOLOGICAL EFFECTS RELATIONSHIPS 4.1
4.1 INTRODUCTION 4.1
4.2 RELATIONSHIPS AMONG CONTAMINANTS, TOXICITY, AND BENTHIC
EFFECTS 4.1
4.2.1 Correlation of Indicators 4.2
4.2.2 Apparent Chemical Effect Thresholds 4.3
4.2.3 Correspondence Among Chemical, Toxicity, and
Benthic Effects Gradients 4.21
4.2.4 Summary 4.29
4.3 COMPARISON OF BIOASSAY RESPONSES WITH BENTHIC INVERTEBRATE
ASSEMBLAGES 4.34
4.3.1 Correlation of Indicators 4.35
4.3.2 Comparison of Bioassays with Benthic Groupings 4.35
4.3.3 Comparison of Significant Responses 4.35
4.3.4 Summary 4.38
4.4 COMPARISONS OF LESION PREVALENCES IN ENGLISH SOLE WITH
CHEMICAL CONTAMINANTS IN SEDIMENTS 4.38
4.5 RELATIONSHIP BETWEEN BIOACCUMULATION AND SEDIMENT
CONTAMINATION 4.42
4.5.1 Inorganic Substances 4.43
4.5.2 Organic Substances 4.45
4.5.3 Summary 4.48
4.6 RELATIONSHIP BETWEEN BIOACCUMULATION AND FISH HISTO-
PATHOLOGY 4.48
4.6.1 Inorganic Substances 4.48
4.6.2 Organic Substances 4.50
4.6.3 Summary 4.52
5.0 PUBLIC HEALTH ASSESSMENT 5.1
5.1 INTRODUCTION 5.1
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5.2 SUMMARY OF RESULTS 5.1
5.2.1 Carcinogens in Fish Muscle Tissue 5.2
5.2.2 Noncarcinogens in Fish Muscle Tissue 5.4
5.2.3 Carcinogens in Crab Muscle Tissue 5.4
5.2.4 Noncarcinogens in Crab Muscle Tissue 5.6
5.2.5 Consumption of Fish Livers 5.6
6.0 PRIORITIZATION OF PROBLEM AREAS AND CONTAMINANTS 6.1
6.1 INTRODUCTION 6.1
6.2 IDENTIFICATION OF PROBLEM AREAS 6.1
6.2.1 Action Assessment Matrices 6.1
6.2.2 Application of Action Levels to Determine Problem
Areas 6.11
6.2.3 Ranking of Study Areas and Segments 6.11
6.3 SPATIAL EXTENT AND RANKING OF PROBLEM AREAS 6.19
6.4 CHEMICAL CHARACTERIZATION OF PROBLEM AREAS 6.25
6.4.1 Hylebos Waterway 6.26
6.4.2 Blair Waterway 6.27
6.4.3 Sitcum Waterway 6.28
6.4.4 Milwaukee Waterway 6.28
6.4.5 St. Paul Waterway 6.28
6.4.6 Middle Waterway 6.29
6.4.7 City Waterway 6.29
6.4.8 Ruston-Pt. Defiance Shoreline 6.30
6.5 RANKING OF POTENTIAL PROBLEM CHEMICALS IN PROBLEM AREAS 6.31
6.6 SUMMARY 6.37
vi
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CONTENTS VOLUME 2
7.0 SOURCE EVALUATION
7.1 INTRODUCTION
7.2 HYLEBOS WATERWAY
7.2.1 Introduction
7.2.2 Contaminants of Concern
7.2.3 Polychlorinated Biphenyls
7.2.4 Aromatic Hydrocarbons
7.2.5 Dibenzofuran
7.2.6 Benzyl Alcohol
7.2.7 Chlorinated Hydrocarbons
7.2.8 Pentachlorocyclopentane Isomer
7.2.9 Arsenic
7.2.10 Copper, Lead, and Zinc
7.2.11 Mercury
7.2,12 Hylebos Waterway: Summary and Recommendations
7.3 SITCUM WATERWAY
7.3.1 Introduction
7.3.2 Aromatic Hydrocarbons and Dibenzofuran
7.3.3 Metals
7.4 ST. PAUL WATERWAY
7.4.1 Introduction
7.4.2 Spatial Distribution
7.4.3 Loading Estimates
7.4.4 Source Identification
7.4.5 Summary and Recommendations
7.5 MIDDLE WATERWAY
7.5.1 Introduction
7.5.2 Pentachlorophenol and Dichlorobenzenes
7.5.3 Aromatic Hydrocarbons and Dibenzofuran
7.5.4 Mercury and Copper
7.5.5 Middle Waterway: Summary and Recommendations
7.6 CITY WATERWAY
7.6.1 Introduction
7.6.2 Contaminants of Concern
7.6.3 Organic Enrichment
vii
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7.6.4 Aromatic Hydrocarbons and Dibenzofuran
7.6.5 Dichlorobenzenes
7.6.6 4-Methylphenol
7.6.7 Polychlorinated Biphenyls
7.6.8 Copper and Zinc
7.6.9 Lead
7.6.10 Summary and Recommendations
7.7 RUSTON-PT. DEFIANCE SHORELINE
7.7.1 Introduction
7.7.2 Spatial Distribution
7.7.3 Loading Estimates
7.7.4 Source Identification
7.7.5 Summary and Recommendations
8.0 RECOMMENDATIONS OF AREAS AND SOURCES FOR POTENTIAL REMEDIAL
ACTIONS
8.1 INTRODUCTION
8.2 RECOMMENDATIONS FOR REMEDIAL ACTION
8.2.1 Hylebos Waterway
8.2.2 Siteurn Waterway
8.2.3 St. Paul Waterway
8.2.4 Middle Waterway
8.2.5 City Waterway
8.2.6 Ruston - Pt. Defiance Shoreline
8.3 GENERAL RECOMMENDATIONS
9.0 OVERVIEW OF CONTAMINATION AND BIOLOGICAL EFFECTS IN
COMMENCEMENT BAY
10.0 STUDY DESIGN EVALUATION AND RECOMMENDATIONS FOR FUTURE STUDIES
11.0 REFERENCES
viii
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FIGURES
Number Page
1.1 General location of study area in Puget Sound 1.2
1.2 South and southcentral Puget Sound showing locations of
Commencement Bay and Carr Inlet 1.3
1.3 Commencement Bay Nearshore/Tideflats study area 1.5
2.1 Locations of Commencement Bay stations sampled for surficial
sediment chemistry during March 2.3
2.2 Locations of Commencement Bay stations sampled for sediment
chemistry during January and July 2.5
2.3 Locations of Commencement Bay stations sampled for sub-
surface sediment chemistry during March and July 2.7
2.4 Locations of Commencement Bay stations sampled for water
column chemistry during April and August 2.9
2.5 Locations of Commencement Bay stations sampled for benthic
macroinvertebrates and sediment bioassays during March and
July 2.10
2.6 Locations of Commencement Bay stations sampled for fish
histopathology and bioaccumulation during June 2.12
2.7 Locations of reference stations sampled in Carr Inlet 2.14
2.8 Examples of surficial sediment chemistry data 2.54
2.9 Example of sediment core data illustrating concentrations
of PAH with depth in sediment at a site within Hylebos
' Waterway 2.56
2.10 Examples of procedures used in calculating average discharge
loads 2.58
3.1 Total average percent fine-grained material (>4 phi) and
average percent clay (>8 phi) in sediments from Commencement
Bay and Carr Inlet study areas 3.2
3.2 Total average oil and grease concentrations in sediments
from Commencement Bay and Carr Inlet study areas 3.3
IX
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3.3 Relative concentrations of sediment organic carbon and
sulfides in Commencement Bay study areas (January and
March, 1984) 3.4
3.4 Comparison of the average percent total volatile solids
with average percent total organic carbon in sediments
from Commencement Bay and Carr Inlet study areas 3.6
3.5 Comparison of the average atomic carbon/nitrogen ratio
(C/N) in sediments from Commencement Bay and Carr Inlet
study areas 3.7
3.6 Area segments defined for Commencement Bay Superfund
data analysis 3.40
3.7 Elevations above reference (EAR) for Pb, Cu, Zn in
Commencement Bay study areas 3.52
3.8 Elevations above reference (EAR) for arsenic in Commencement
Bay study areas 3.53
3.9 Elevations above reference (EAR) for low molecular weight
aromatic hydrocarbons in Commencement Bay study areas 3.54
3.10 Elevations above reference (EAR) for high molecular weight
aromatic hydrocarbons in Commencement Bay study areas 3.55
3.11 Elevations above reference (EAR) for total PCBs in
Commencement Bay study areas 3.56
3.12 Elevations above reference (EAR) for total chlorinated
benzenes in Commencement Bay study areas 3.57
3.13 Elevations above reference (EAR) for total chlorinated
butadienes in Commencement Bay study areas 3.58
3.14 Elevations above reference (EAR) for total phthalates in
Commencement Bay study areas 3.59
3.15 Elevations above reference (EAR) for Pb, Cu, Zn by segment
in Commencement Bay study areas 3.61
3.16 Elevations above reference (EAR) for arsenic by segment in
Commencement Bay study areas 3.62
3.17 Elevations above reference (EAR) for low molecular weight
aromatic hydrocarbons by segment in Commencement Bay study
areas 3.63
3.18 Elevations above reference (EAR) for high molecular weight
aromatic hydrocarbons by segment in Commencement Bay study
areas 3.64
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3.19 Elevations above reference (EAR) for total PCBs by segment
in Commencement Bay study areas 3.65
3.20 Elevations above reference (EAR) for total chlorinated
benzenes by segment in Commencement Bay study areas 3.66
3.21 Elevations above reference (EAR) for total chlorinated
butadienes by segment in Commencement Bay study area 3.67
3.22 Elevations above reference (EAR) for total phthalates by
segment in Commencement Bay study areas 3.68
3.23 Mean number of species per grab sample and mean number of
individuals/m2 in each study area 3.81
3.24 Mean number of polychaete species per grab sample and
mean number of polychaete individuals/m2 in each survey
area 3.84
3.25 Mean number of mollusc species per grab sample and mean
number of mollusc individuals/m2 in each survey area 3.85
3.26 Mean number of crustacean species per grab sample and
mean number of crustacean individuals/m? in each survey
area 3.86
3.27 Mean number of echinoderm species per grab sample and
mean number of echinoderm individuals/m2 in each study
area 3.88
3.28 Mean abundances per station of the five numerically dominant
species per study area and the proportions of total infaunal
abundances for which they account 3.89
3.29 Total abundances of numerically dominant species at
stations in Hylebos Waterway, and the proportions of
total infaunal abundances for which they account 3.93
3.30 Total abundances of numerically dominant species at
stations in Blair, Sitcum, and Milwaukee Waterways, and
the proportions of total infaunal abundances for which
they account 3.94
3.31 Total abundances of numerically dominant species at stations
in St. Paul, Middle, and City Waterways, and the proportions
of total infaunal abundances for which they account 3.95
3.32 Total abundances of the numerically dominant species at
stations along the Ruston-Pt. Defiance Shoreline and in
Carr Inlet and the proportions of total infaunal abundances
for which they account 3.96
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3.33 Results of a Q-mode classification analysis (Bray-Curtis
similarity index, group average clustering strategy) using
square-root transformed abundances of the 64 numerically
dominant infaunal species 3.100
3.34 Geographic distribution of station groups 1-9, plus outliers
(o), in Commencement Bay waterways (from Figure 3.33) 3.101
3.35 Sediment grain size characteristics of the major station
groups defined by normal classification analysis of the
benthic infaunal data in Commencement Bay study areas 3.103
3.36 Geographic distribution of sediment volatile solids content 3.107
3.37 Total organic carbon content of the sediments in Hylebos
Waterway 3.109
3.38 Total organic carbon content of the sediment in Blair
Waterway 3.110
3.39 Total organic carbon content of the sediments in City
Waterway 3.111
3.40 Percent fine-grained materials (silt plus clay) in the
sediments of Hylebos Waterway 3.112
3.41 Percent fine-grained materials (silt plus clay) in the
sediments of Blair Waterway 3.113
3.42 Percent fine-grained materials (silt plus clay) in the
sediments of City Waterway 3.114
3.43 Correlations of numerical abundances of all benthic infauna,
polychaetous annelids, and molluscs vs. the percent of fine-
grained materials (silt plus clay) in the sediments 3.115
3.44 Summary of spatial patterns of benthic depressions 3.124
3.45 Bioassay responses to sediments from Hylebos and Blair
Waterways 3.135
3.46' Bioassay responses to sediments from Middle, Milwaukee,
Sitcum, St. Paul, and City Waterways 3.136
3.47 Bioassay responses to sediments from Ruston-Pt. Defiance
Shoreline and Carr Inlet 3.137
3.48 Relationship between amphipod and oyster larvae bioassay
results 3.138
3.49 Summary of spatial patterns of significant bioassay
responses 3.141
xn
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3.50 Comparisons of major characteristics of fish assemblages
from Commencement Bay study areas with those of the
assemblage from Carr Inlet 3.144
3.51 Length frequency distributions of English sole captured
in Carr Inlet and Commencement Bay 3.145
3.52 Comparison of abundances of English sole from Commencement
Bay study areas with the abundance from Carr Inlet 3.147
3.53 Comparison of male percentages of English sole populations
with fine-grained sediment fractions (silt plus clay) using
the Spearman rank correlation coefficient (rs) 3.148
3.54 Comparison of weight-length relationships of male and
female English sole captured in Commencement Bay and Carr
Inlet 3.150
3.55 Comparisons of length distributions of English sole captured
in City and Sitcum Waterways during 1981 and 1984 using the
Mann-Whitney U-test 3.152
3.56 Comparisons of prevalences of four liver disorders with age
of English sole from Commencement Bay using the Spearman
rank correlation coefficient (rs) 3.158
3.57 Comparisons of prevalences of six liver disorders between
English sole from Commencement Bay and Carr Inlet using a
2x2 contingency test 3.160
3.58 Comparisons of prevalences of one or more of four major
hepatic lesions in English sole from Commencement Bay and
Carr Inlet using a 2 x 2 contingency test 3.165
3.59 Comparison of prevalences of hepatic lesions in English
sole sampled in the present study and in Mai ins et al.
(1984) 3.168
3.60 Summary of areas having significantly elevated prevalences
of one or more hepatic lesions in English sole 3.171
3.61 Concentrations of hexachlorobutadiene and hexachlorobenzene
in English sole muscle tissue 3.181
3.62 Concentrations of tetrachloroethylene in English sole
muscle tissue 3.182
3.63 Concentrations of pentachlorophenol and 1,3-dichlorobenzene
in English sole muscle tissue 3.183
3.64 Concentrations of naphthalene in English sole muscle tissue 3.184
3.65 Concentrations of di-n-butyl phthalate in English sole
muscle tissue 3.185
x i i i
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3.66 Concentrations of bis(2-ethylhexyl) phthalate in English
sole muscle tissue 3.186
3.67 Concentrations of total PCBs in English sole muscle tissue 3.187
4.1 Correlation patterns among selected contaminants, sediment
toxicity, and benthic effects 4.4
4.2 Example use of synoptic benthic effects and sediment
toxicity data to determine apparent chemical effect
thresholds 4.5
4.3 Correlation plots of sediment toxicity indicators and
selected chemicals at Hylebos Waterway cross-channel
biology stations (HY-22, HY-23, HY-24, and HY-42, HY-43,
and HY-44) 4.23
4.4 Correlation plots of benthic indicators and selected
chemicals at Hylebos Waterway cross-channel stations
(HY-22, HY-23, HY-24) 4.25
4.5 Correlation plots of sediment toxicity indicators and
selected chemicals at St. Paul Waterway stations (SP-11,
SP-12, SP-14, SP-15, and SP-16) 4.27
4.6 Correlation plots of benthic indicators and selected
chemicals at St. Paul Waterway stations (SP-11, SP-12,
SP-14, SP-15, and SP-16) 4.28
4.7 Correlation plots of sediment toxicity indicators and
selected chemicals at the head of City Waterway (Stations
CI-11, CI-13, and CI-17) 4.30
4.8 Correlation plots of benthic indicators and selected
chemicals at the head of City Waterway (Stations CI-11,
CI-13, and CI-17) 4.31
4.9 Correlation plots of sediment toxicity indicators and
selected chemicals along a Ruston-Pt. Defiance offshore
transect of stations (RS-18, RS-19, and RS-20) 4.32
4.10 Correlation plots of benthic indicators and selected
chemicals along a Ruston-Pt. Defiance offshore transect of
stations (RS-18, RS-19, and RS-20) 4.33
4.11 Ranges of bioassay responses for the station groupings
based on classification analysis of benthic assemblages 4.37
4.12 Correspondence between stations having significant (P<0.05)
bioassay responses and stations having significant (P<0.05)
benthic depressions 4.39
xiv
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4.13 Correlations of lesion prevalence in English sole with
sediment concentrations of PAH and metals. ns=P>0.95,
experimentwise 4.40
4.14 Correlations of lesion prevalences in English sole with
sediment concentrations of PCBs, chlorinated benzenes, and
phthalates. ns=P>0.05, experimentwise 4.41
4.15 Relationship of sediment contamination to bioaccumulation
in English sole in Hylebos Waterway. EAR is the ratio of
contaminant concentrations in Hylebos Waterway to those in
Carr Inlet 4.44
4.16 Relationship of PCB contamination of sediments and fish
muscle tissue for Commencement Bay waterways 4.47
6.1 Evaluation and prioritization of problem areas and
chemicals 6.2
6.2 Relative ranking of study area segments by average and
maximum observed contamination, toxicity, and biological
effects 6.20
6.3 Definition and prioritization of Commencement Bay problem
areas 6.23
6.4 Prioritization of chemicals 6.32
xv
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TABLES
Number Page
2.1 Summary of general study design 2.2
2.2 Mean water depths by study area for benthic infauna
stations 2.15
2.3 Summary of available precision and recovery data for
Commencement Bay organic chemistry samples 2.42
2.4 Summary of available precision and recovery data for
Commencement Bay inorganic chemistry samples 2.43
2.5 Population exposed by consumption rate 2.46
2.6 Fish liver consumption rates 2.48
2.7 A summary of health effects data for carcinogens and
noncarcinogens 2.49
3.1 Concentrations of U.S. EPA priority pollutant trace
metals and additional metals in surface sediments
(0-2 cm) from Commencement Bay and Carr Inlet 3.15
3.2 U.S. EPA priority pollutant trace metals and additional
metals in subsurface sediments from Commencement Bay 3.16
3.3 Summary of metal concentrations in sediments from Puget
Sound reference areas 3.18
3.4 Comparison of the range in elevations above reference
(EAR) for inorganic contaminants of concern in surface
sediments (0-2 cm) from Commencement Bay 3.19
3.5 Concentrations of U.S. EPA organic priority pollutants
and additional hazardous substance list (HSL) compounds
in surface sediments (0-2 cm) from Commencement Bay and
Carr Inlet 3.21
3.6 Concentrations of tentatively identified compounds in
surface sediments (0-2 cm) from Commencement Bay and
Carr Inlet 3.26
3.7 U.S. EPA organic priority pollutants and additional
hazardous substance list (HSL) compounds in subsurface
sediments from Commencement Bay 3.28
xvi
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3.8 Organic compounds with at least a fivefold difference
between maximum subsurface and surface sediment
concentrations 3.32
3.9 Summary of organic compound concentrations in sediments
from Puget Sound reference areas 3.34
3.10 Comparison of the range in elevations above reference
(EAR) for organic contaminants of concern in surface
sediments from Commencement Bay 3.37
3.11 Commencement Bay area segments used for data analysis 3.42
3.12 Summary of chemicals with elevations above reference
greater than 1,OOOX in sediments from Commencement Bay 3.46
3.13 Summary of chemicals with elevations above reference
between 100 and 1,OOOX in sediments from Commencement
Bay stations 3.48
3.14 Summary of chemicals with sediment elevations above
reference (EAR) between 100 and l.OOOX averaged over
Commencement Bay areas or segments 3.50
3.15 Station locations at which sediment concentrations of
chemicals exceeded 80 percent of sediment concentrations
measured in all Commencement Bay study areas 3.74
3.16 Abundances and ranks of the 10 numerically dominant
benthic taxa collected in Commencement Bay 3.79
3.17 Results of Kruskal-Wallis tests comparing numbers of
taxa per grab sample and numbers of individuals per
grab sample among the study areas 3.82
3.18 Results of Mann-Whitney U-test multiple comparisons
of numbers of taxa per grab sample and numbers of
individuals per grab sample among the study areas 3.83
3.19 Key for Figure 3.28 3.90
3.20 Numbers of amphipods collected at each of the
Commencement Bay stations (0.24 m2) sampled in March, 1984 3.91
3.21 Key for Figures 3.29 - 3.32 3.97
3.22 Mean abundances (No./m2) Of numerically dominant taxa
and mean values of sediment characteristics for the
major station groups defined by normal classification
analyses 3.102
xvn
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3.23 Results of Pearson product-moment correlation analyses
between sediment characteristics, and abundances of
major taxonomic groups and numerically dominant taxa
(Ruston-Pt. Defiance Shoreline and Carr Inlet study
areas deleted) 3.116
3.24 Pairings of reference stations and potentially impacted
stations used for statistical comparisons 3.119
3.25 Comparisons of mean abundances of benthic invertebrate
taxa between potentially impacted stations and reference
stations 3.120
3.26 Summary of non-dilution amphipod bioassay results 3.126
3.27 Summary of amphipod sediment dilution bioassays 3.127
3.28 Comparisons of initial and dilution bioassays for
amphipod mortality and oyster larval abnormality 3.128
3.29 Summary of non-dilution oyster larvae bioassay results 3.129
3.30 Summary of oyster larvae sediment dilution bioassays 3.132
3.31 Relative abundances of fishes captured in Commencement
Bay and Carr Inlet 3.142
3.32 Comparisons of sex distributions of Commencement Bay
English sole having various kinds of liver lesion with
the sex distribution of all English sole sampled in
Commencement Bay 3.156
3.33 Comparisons of prevalences of four liver lesions between
English sole from study areas in Commencement Bay and
Carr Inlet 3.161
3.34 Comparisons of prevalences of four liver lesions between
English sole from trawl transects in Commencement Bay
and Carr Inlet 3.163
3.35 Comparisons of weight-length regression coefficients
between English sole with lesions and conspecifics
without lesions 3.166
3.36 Mean concentrations (mg/kg wet weight) of inorganic
tissue substances in English sole muscle tissue 3.173
3.37 Mean concentrations (mg/kg wet weight) of inorganic
substances in crab muscle tissue 3.175
3.38 U.S. EPA priority pollutants not detected in any fish
or crab muscle tissue sample at any of 17 trawl
transects 3.176
xvm
-------
3.39 Concentrations (ug/kg wet weight) of organic compounds
in English sole muscle tissue at all 17 trawl transects 3.180
3.40 Concentrations of p,p'-DDE in English sole muscle tissue 3.189
3.41 Total extractable organic material in English sole
muscle tissue 3.192
3.42 Age composition of English sole samples used for bio-
accumulation analyses 3.194
3.43 Concentrations (ug/kg wet weight) of selected organic
compounds in crab muscle tissue 3.196
3.44 Concentrations (mg/kg wet weight) of metals in
Commencement Bay in English sole muscle tissue as
determined by Gahler et al. (1982) 3.197
3.45 Concentrations (ug/kg wet weight) of PCBs and hexa-
chlorobenzene in fish muscle tissue in Hylebos and
City Waterways as determined by Gahler et al. (1982) 3.199
4.1 Apparent effect thresholds for potential problem metals
normalized to dry weight 4.8
4.2 Apparent effect thresholds for potential problem organic
compounds normalized to dry weight 4.9
4.3 Apparent effect thresholds for conventional variables 4.10
4.4 Summary of effects and potential problem chemicals at
biological stations (normalized to dry weight) 4.11
4.5 Apparent effect thresholds for potential problem metals
normalized to organic carbon 4.14
4.6 Apparent effect thresholds for potential problem organic
compounds normalized to organic carbon 4.15
4.7 Summary of effects and potential problem chemicals at
biological stations (normalized to organic carbon) 4.16
4.8 Apparent effect thresholds for potential problem metals
normalized to fine-grained material 4.17
4.9 Apparent effect thresholds for potential problem organic
compounds normalized to fine-grained material 4.18
4.10 Summary of effects and potential problem chemicals at
biological stations (normalized to fine-grained
material) 4.19
xix
-------
4.11 Chemicals of concern with concentrations never exceeding
apparent effect thresholds ' 4.22
4.12 Correlations of abundances of major benthic invertebrate
taxa with amphipod mortality and oyster larvae abnor-
mality 4.36
4.13 Average metal concentrations (mg/kg wet weight) in
English sole composite liver samples 4.49
4.14 Total PCB concentrations (ug/kg wet weight) in English
sole composite liver samples 4.51
4.15 Occurrences of major hepatic lesions relative to muscle
tissue PCB levels in English sole from Commencement Bay 4.53
5.1 Estimated individual lifetime risks for organic compounds
in fish muscle tissue 5.3
5.2 Projected lifetime cancer cases for PCBs and arsenic 5.5
6.1 Action assessment matrix of sediment contamination,
sediment toxicity, and biological effects indices for
Commencement Bay study areas, by study area 6.3
6.2 Action assessment matrix of sediment contamination,
sediment toxicity, and biological effects indices for
Commencement Bay study areas, Hylebos segments 6.5
6.3 Action assessment matrix of sediment contamination,
sediment toxicity, and biological effects indices for
Commencement Bay study areas, Blair segments 6.6
6.4 Action assessment matrix of sediment contamination,
sediment toxicity, and biological effects indices for
Commencement Bay study areas, City segments 6.7
6.5 Action assessment matrix of sediment contamination,
sediment toxicity, and biological effects indices for
Commencement Bay study areas, Ruston segments 6.8
6.6 Mean reference values used to calculate elevations
above reference for benthic infauna 6.9
6.7 Identification of reference groups used to calculate
benthic abundance elevations above reference for study
areas and segments 6.10
6.8 Action-level guidelines 6.12
6.9 Summary of ranking criteria for sediment contamination,
toxicity, and biological effects indicators 6.14
-------
6.10 Ranking of study areas and segments by average magni-
tude and number of significant sediment contaminants 6.16
6.11 Ranking of study areas and segments by the average
magnitude of sediment toxicity and biological effects 6.17
6.12 Ranking of study area segments by maximum observed
sediment contamination, toxicity, and biological
effects 6.18
6.13 Definition and relative ranking of problem areas 6.21
6.14 Potential problem chemicals in problem areas 6.34
xxi
-------
ACKNOWLEDGEMENTS
This document was compiled by Tetra Tech, Inc., under the direction
of Dr. Thomas C. Ginn, for the State of Washington Department of Ecology
(WDOE) in partial fulfillment of Contract No. C-84031 for the Commencement
Bay Nearshore/Tideflats Area Superfund Project. Mr. James D. Krull of
the WDOE was the Project Manager. Mr. Larry Marx provided project coordination
for Tetra Tech, as did Ms. Mary Ruckelshaus for WDOE. Mr. Charles Kleeburg
and Mr. Robert Kievit were the U.S. EPA Region X project monitors. The
work was conducted under an EPA/State Cooperative Agreement (No. CX810926-01-0).
The primary authors of this report were Mr. Robert Barrick, Dr. Scott
Becker, Dr. Donald Weston, and Dr. Thomas Ginn. Individuals contributing
to the sampling, data analysis, and report writing efforts are listed below.
Tetra Tech, Inc. Technical Staff
Ms. Ann K. Bailey
Mr. Robert C. Barrick
Dr. D. Scott Becker
Dr. Gordon R. Bilyard
Ms. Marcy B. Brooks-McAuliffe
Ms. Roberta P. Feins
Dr. Thomas C. Ginn
Mr. Thomas Grieb
Dr. Marc W. Lorenzen
Mr. Larry Marx
Ms. Nancy A. Musgrove
Dr. Robert A. Pastorok
Ms. Glynda Steiner
Mr. Jeff Stern
Dr. Michael Swayne
Mr. Gary Weins, P.E.
Ms. Julia F. Wilcox
Dr. Les G. Williams
Production Staff
Mr. A. Brian Carr
Ms. Betty Dowd
Ms. Lisa M. Fosse
Ms. Gretchen Margrave
Ms. Sharon L. Hinton
Ms. Karen L. Keeley
Ms. Dana L. Schai
Chemistry Quality Assurance
Chemistry Quality Assurance,
Field Sampling, Data Analysis,
Decision-Making Approach
Field Sampling, Fish and Shellfish,
Data Analysis
Benthic Infauna, Data Analysis
Technical Editor
Database Management
Management, Data Analysis, Endanger-
ment Assessment, Decision-Making
Approach
Data Analysis, Statistics
Management, Quality Control, Review
Health and Safety, Project Coordination
Database Management
Study Design, Field Sampling
Source Identification
Field Sampling, Data Analysis
Database Management
Source Evaluations
Chemistry Quality Assurance
Bioassays, Data Analysis
Graphics
Graphics
Word Processing
Word Processing
Word Processing
Graphics
Word Processing
xxn
-------
Ms. Gail Singer
Ms. Gestin K. Suttle
Ms. Stephanie Turco
Word Processing
Word Processing
Reproduction
University of Washington/Evans Hamilton, Inc.
Mr. Jack Q. Word
Mr. Keven Li
Mr. Jeff Ward
Ms. Karen L. Keeley
Ms. Julia L. Schroeder
EVS Consultants
Dr. Robert N. Dexter
Dr. Peter Chapman
Raven Systems and Research Inc.
Mr. John Dermody
Mr. Michael Healey
Fishi and Wildlife Health Consultants
Dr. Marsha Landolt
Dr. Richard Kocan
Mr. Dave Powell
JRB Associates (SAIC)
Dr. Don Weston
Mr. Richard Greiling
Ms. Barbara Morson
Ms. Patricia 0'Flaherty
AB Consultants
Ms. Ann K. Bailey
Versar, Inc.
Mr. Douglas A. Dixon
Ms. Gena Dixon
Mr. Walt Palmer
Tacoma Pierce County Health Department
Mr. Douglas Pierce
Mr. James Mitchell
Mr. Thomas Rogers
Benthic Sampling Supervision, Benthic
Data Interpretation
Benthic Taxonomy
Benthic Taxonomy
Benthic Taxonomy
Benthic Taxonomy
Field Supervision, Data Interpretation
Bioassays
Field Mobilization, Geophysics
Field Mobilization, Geophysics
Fish Pathology
Fish Pathology
Fish Pathology
Source Identification
Source Identification
Source Identification
Source Identification
Quality Assurance
Endangerment Assessment
Endangerment Assessment
Endangerment Assessment
Community Relations
Drainage Maps
Drainage Survey
xxi ii
-------
Washington Department of Ecology-Water Quality Investigations Section
Mr. William Yake Source Investigation
Mr. Art Johnson Source Investigation
Mr. Dale Norton Source Investigation
Others
Mr. Wayne Palsson Field Sampling
Ms. Ruth Mandapat Fish Aging
Dr. Richard Branchflower Toxicology, Risk Assessment
Dr. John Hedges Chemical Analyses, Suspended Particu-
lates
Appreciation is also extended to the U.S. Environmental Protection
Agency's (EPA) Superfund Contract Laboratory Program for analytical support,
to the U.S. EPA Region X/WDOE Manchester Laboratory for analytical support,
and to U.S. EPA Region X for quality assurance support. We also appreciate
the assistance of Mr. Charles Eaton, Skipper of the R/V Kittiwake, in conducting
the field sampling for benthos and fishes, and Mr. Benjamin Huntley, Skipper
of the M/V Readout and the M/V Cathlamet Bay, in conducting the field sampling
for sediment cores and suspended solids.
Preparation of this report was aided greatly by the support and construc-
tive contributions of the WDOE management staff, the Technical Oversight
Committee, the Citizens Advisory Committee and many personnel from federal,
state, industry, and environmental organizations.
The following individuals provided written comments on all parts of
the draft report:
Dr. Roy Carpenter (U of W)
Dr. Sin-Lam Chan (NOAA, NMFS)
Mr. Joseph Cummins (U.S. EPA)
Mr. Thomas Deming (Puyallup Tribe)
Mr. James Ebbert (USGS)
Dr. Dave Jamison (WDNR)
Mr. Ed Long (NOAA, OAD)
Mr. Rick Pierce (WDOE)
Ms. Diane Robbins
Dr. Donald Schults (U.S. EPA, ORD)
Mr. William Wilkerson (WDF)
The helpful criticisms from these reviewers are gratefully acknowledged.
xxiv
-------
1.0 INTRODUCTION
1.1 BACKGROUND
In December, 1980, in response to significant public health and environ-
mental threats associated with the release of hazardous substances from
uncontrolled waste sites and from chemical spills. Congress passed the
Comprehensive Environmental Response, Compensation and Liability Act (CERCLA).
One result of CERCLA was the establishment of a "Superfund" to finance
investigations of the hazardous waste problem and to fund investigations
and cleanup of the most seriously contaminated sites. The U.S. Environmental
Protection Agency (U.S. EPA) was delegated the lead role to work with state
and local agencies to coordinate and implement programs authorized by CERCLA.
On October 23, 1981, the U.S. EPA announced an "interim priority list"
of 115 top-priority hazardous waste sites targeted for action under Superfund.
Commencement Bay, located in the southern Puget Sound region, was listed
as the highest priority site in the state of Washington and one of the
10 highest national priority sites federal funding of remedial action under
CERCLA. The Corrmencement Bay site was divided into four areas: the Deepwater,
the Nearshore, the Tideflats Industrial, and the South Tacoma channel.
On December 30, 1982, U.S. EPA proposed additions to the national
priority list. The list increased to 418 hazardous waste sites ranked
by their potential threat to public health and the environment. On this
subsequent Superfund list, the Nearshore and the Tideflats Industrial areas
were designated as a separate project, as was the South Tacoma channel,
The Deepwater area was eliminated as a priority site because water quality
studies indicated less contamination in that area than was initially suspected.
On September 6, 1983, U.S. EPA published and promulgated the first official
National Priority List (NPL) of 406 hazardous waste sites, including the
Commencement Bay Nearshore/Tideflats area.
On April 13, 1983, U.S. EPA announced that an agreement was reached
with the Washington Department of Ecology (WDOE) to conduct a remedial
investigation of the hazardous substance contamination in the Nearshore/
Tideflats Industrial areas of Commencement Bay. Under the Cooperative
Agreement, the WDOE was delegated the lead role in the investigation.
1.2 SITE DESCRIPTION
Commencement Bay is an embayment of approximately 9 mi^ in southern
Puget Sound, Washington (Figures 1.1 and 1.2). The bay opens to Puget Sound
in the northwest, with Tacoma situated on the south and southeast shores.
The mean tidal range in Commencement Bay is 8.1 ft, with a diurnal range
of 11.8 ft and an extreme range of 19 ft (COE 1983). Residential portions
of northeast Tacoma and the Browns Point section of Pierce County occupy
the north shore of the bay. Ownership of the shoreline is vested in the
Port of Tacoma, the city of Tacoma, Pierce County, the state of Washington,
1.1
-------
0 10 -20
I I I MILES
[ [ 1 KILOMETERS
0 10 20
Figure 1.1. General location of study area in Puget Sound.
1.2
-------
OJ
Figure 1.2. South and southcentral Puget Sound showing locations of Commencement Bay
and Carr Inlet.
-------
the Puyallup Indian Tribe, and numerous private parties. Much of the publicly
owned land is leased to private industrial and commercial enterprises.
The Nearshore area is defined as the area along the Ruston Way shoreline
from the head of City Waterway to Pt. Defiance, including all waters with
depths less than 60 ft. The Tideflats area includes Hylebos Waterway,
Blair Waterway, Sitcum Waterway, Milwaukee Waterway, St. Paul Waterway,
Middle Waterway, City Waterway, and the Puyallup River upstream to the
1-5 highway bridge (Figure 1.3). The project boundaries are shown in Figure
X • j *
1.3 NATURE AND EXTENT OF PROBLEM
Urbanization and industrial development of the Commencement Bay area
began in the late 1800s. At that time, the south end of the bay was primarily
tideflats formed by the Puyallup River delta. Since their inception in
the 1920s, dredge and fill activities have significantly altered the estuarine
nature of the bay. Intertidal areas were covered and meandering streams
and rivers were channelized. Numerous industrial and commercial operations
located in the newly filled areas of the bay. These included pulp and
lumber mills, shipbuilding, shipping, marinas, chlorine and chemical production,
concrete production, aluminum smelting, oil refining, food processing,
automotive repair services, railroad operations, and a number of other
storage, transportation, and chemical manufacturing companies. Tne documented
waste management practices of these operations included landfills, open
dumps, chemical recycling and reclamation, and on-site storage and treatment
facilities.
A smelter (ASARCO) has been located in the nearshore area close to
Ruston since the late 1800s. The plant, operational until March, 1985,
generated substantial amounts of slag containing various metals. This
slag was deposited along the shoreline near the plant and used as fill,
riprap, and ballast material in the Tideflats area. The slag material
was also utilized to produce commercial sandblasting material used widely
throughout the study area. While the hazards of the slag remain undetermined,
it contains high concentrations of toxic metals, primarily arsenic.
Since initial industrialization of the Commencement Bay area, hazardous
substances and waste materials have been released into the terrestrial,
freshwater, groundwater, and marine environments. Discharges and dumping
of solid and liquid, organic and inorganic waste materials, and contamination
from airborne wastes entering via surface and groundwaters have modified
the chemical quality of the waters and sediments in many portions of the
area. These pollutants include metals (e.g., arsenic, lead, zinc, copper,
mercury) and organic compounds [e.g., polychlorinated biphenyls (PCBs),
dibenzofurans, chlorinated pesticides, plasticizers (phthalates) , and
polynuclear aromatic hydrocarbons (PAH)].
Pollutant loadings in the Commencement Bay site originate from both
point and nonpoint sources. Industrial surveys conducted by the Tacoma-Pierce
County Health Department and the Port of Tacoma indicate that there are
over 281 industrial activities in the Commencement Bay Nearshore/Tideflats
area. Approximately 27 of these are NPDES-permitted discharges, including
two sewage treatment plants. Nonpoint sources include two creeks; the
1.4
-------
COMMENCEMENT
BAY
0
I
J NAUTICAL MILES
I
0
KILOMETERS
Figure 1.3. Commencement Bay Nearshore/Tideflats study area.
-------
Puyallup River; numerous storm drains, seeps, and open channels; groundwater
seepage; atmospheric fallout; and spills. The Tacoma-Pierce County Health
Department summarized point and nonpoint sources in 1983, identifying 334 drains
(pipes), seeps, and open channels that empty into the Nearshore/Tideflats
area (Rogers et al. 1983). Recent investigations by regulatory agencies
have identified 429 additional point and nonpoint discharges in the study
area. All known discharges were assigned an identifier with their locations
and description and were compiled in the project database (Tetra Tech 1985).
Previous investigations of the nearshore waters of Commencement Bay
demonstrated the existence of sediment contamination by toxic pollutants,
accumulation of some of these substances by biota, and possible pollution-
associated abnormalities in indigenous biota (Crecelius et al. 1975; Riley
et al. 1980, 1981; Mai ins et al. 1980, 1982; Gahler et al. 1982). These
studies indicate that the highest concentrations of certain metals (arsenic,
copper, lead, mercury) were found in sediments in the waterways, along
the southwest shore, and near the ASARCO smelter. Sediment contamination
by persistent organic compounds (e.g., PCBs) was detected in the heavily
industrialized waterways and along the Ruston-Pt. Defiance Shoreline.
The toxicity of Commencement Bay sediments to infaunal amphipods was
studied using acute bioassays (Swartz et al. 1982a,b). The waterways contain
both highly toxic and nontoxic sediments with heterogenous spatial distribu-
tions. Sediments with the highest toxicity were detected near docks, drains,
and ditches, which are most likely associated with pollutant sources.
In the waterways, higher toxicities were observed in intertidal sediments
compared with those from midchannel and subtidal sites.
Commencement Bay, like much of the Puget Sound system, supports important
fishery resources, especially anadromous salmonid populations. Although
occupying Commencement Bay for only part of their life cycle, these species
have critical estuarine migratory and rearing habitat requirements. The
Commencement Bay area also supports recreational fisheries, including pollock,
hake, rockfish, and cod. In addition, many of the other important fishes
and invertebrates (e.g., English sole and crab) live in contact with the
bottom sediments, resulting in a high potential for uptake of sediment-
associated contaminants. Studies indicate that the incidence of liver
lesions is greatest in fish from areas with high levels of sediment-associated
contaminants (Mai ins et al. 1980). Higher prevalences of abnormalities
have also been found in organs of shrimp and crabs from Commencement Bay
waterways (Mai ins et al. 1980). Concern exists over the potential human
health impacts from consumption of local seafood organisms that contain
chemical contaminants. The Tacoma-Pierce County Health Department issued
an advisory on fish consumption in 1982.
1.4 COOPERATIVE AGREEMENT
The general objective of the work planned under the U.S EPA/WDOE
Cooperative Agreement is to identify the worst problems and to provide
a database and framework for future activities. The ultimate goal of the
Superfund project is to remedy public health or environmental threats in
1.6
-------
a prioritized manner. The Remedial Investigation focuses on sediment
contamination, effects on biota, and sources of contamination. The overall
scope of the Remedial Investigation includes the following tasks:
Task 1. Investigative support
Task 2. Development of preliminary remedial objectives
Task 3. Determine type and extent of contamination and exposure
pathways
Task 4. Determine sources of contamination and characterize
as current or historical
Task 5. Endangerment assessment support
Task 6. Identify potential remedial technologies
Task 7. Safety plan, quality assurance/quality control plan.
The key questions to be answered during the Remedial Investigation include:
Is the area contaminated?
Does the contamination result in adverse effects?
Is there a potential threat to public health?
Can the contaminant sources be identified?
What are the potential remedial action alternatives?
Would remedial action reduce the threat to the environment
or to public health?
In order to answer these questions, the following goals and objectives
were set for the Remedial Investigation:
Define a problem sediment
Apply definition of problem sediment in order to delineate
problem areas
Determine problem chemicals for problem areas
Determine problem sources for problem chemicals
Prioritize problem areas, problem chemicals, and problem
sources
Assess impacts of fish and crab consumption on human health
Document alternative methods of dredging, handling, and
disposing of contaminated sediments
• Initiate a decision-making framework for managing the disposal
of contaminated sediments
• Identify potential remedial alternatives.
1.5 REPORT OVERVIEW
This report represents work completed under the U.S. EPA/WDOE Cooperative
Agreement for Task 3 (determine type and extent of contamination and exposure
pathways), Task 4 (determine sources of contamination and characterize
as current and historical sources), and Task 5 [endangerment (public health)
assessment]. The Commencement Bay Superfund Investigation includes various
integrated program components, including assessments of chemical contamination,
biological effects, toxicity, public health concerns, source identification,
and identification of potential remedial actions and technologies. Volume 1
contains Sections 1 through 6. Volume 2 contains Sections 7 through 11.
The methods and results for each individual study component are included
in Sections 2 and 3, respectively, of this report. Section 4 describes
1.7
-------
quantitative relationships among contamination and biological effects that
form the basis for estimating contaminant effect levels. An assessment
of public health risks from consumption of contaminated seafood is included
as Section 5. All of the study results described in Sections 3 through
5 are then integrated into an identification and prioritization of problem
areas in Section 6. Section 7 contains source evaluations for the previously
identified areas and contaminants. High priority areas with identified
sources are recommended for remedial actions in Section 8. An overview
of contamination and biological effects in the entire study area is presented
in Section 9. A retrospsective evaluation of the study design and recommen-
dations for future studies are presented in Section 10. References are
provided in Section 11. All raw data collected as part of the present
study are included in Appendices I-XV.
1.8
-------
2.0 METHODS
2.1 GENERAL APPROACH
2.1.1 Study Design
Field studies for the Commencement Bay Nearshore/Tideflats Remedial
Investigation were designed to document the degree and spatial extent of
chemical contamination, adverse biological effects, and potential threats
to public health. This information was used in conjunction with historical
data to formulate decision criteria which, in turn, were used to identify
problem areas and to prioritize these areas for possible source control
and/or sediment remedial action. This decision-making approach is described
in detail in Tetra Tech (1984a). That document includes rationales for
the selection of chemical and biological variables and examples of the
development and application of the decision criteria.
The general study design for the Commencement Bay project is presented
in Table 2.1. Sediment contamination was measured in two media: bottom
sediments (surface and subsurface) and water column particles. Four kinds
of biological effects of chemical contamination were also measured: alteration
of benthic macroinvertebrate assemblages, toxicity to bioassay organisms
(amphipods and oyster larvae), prevalence of histopathological disorders
in English sole livers, and bioaccumulation (English sole and cancrid crab
muscle tissue, English sole livers). In addition to the data collected
as part of the main Commencement Bay project, contaminant/effects information
was collected in Blair Waterway as part of the Blair Waterway Dredging
Survey, a combined effort between the Port of Tacoma and the Commencement
Bay Superfund project. Because these samples were collected using methods
identical to those of the Commencement Bay project, the resulting data
were included in the analyses in the present report.
2.1.2 Station Locations
Location of stations sampled during the Commencement Bay project are
presented in Figures 2.1-2.7. Locations of the Blair Waterway Dredging
Survey stations are presented in Figures 2.2, 2.3, and 2.5. State plane
coordinates and water depths (corrected to mean lower low water) of all
stations are listed in Appendix XIV. The average water depth of stations
sampled for benthic infauna in each study area is summarized in Table 2.2.
Stations selected for a preliminary survey in January, 1984 (Figures 2.2
and 2.7) were sampled primarily for sediment chemistry, and the resulting
information was used for the following purposes:
• Confirmation of data from previous studies, especially in
areas with little or conflicting data on sediment contam-
ination
• Collection of sediment quality data from project areas that
had not been sampled previously
2.1
-------
TABLE 2.1. SUMMARY OF GENERAL STUDY DESIGN
Number of Stations
Commencement Carr Study Areas3
Variable Bay Inlet Sampled
Sediment Chemistry
Surface
Subsurface
Water Column Chemistry
Benthic Macroinvertebrates
Sediment Bioassays
Fish Histopathology
Bioaccumulation
15
111
12
18
17
9
44
6
46
6
15
15
4C HY,BL,MI,MD,CI,RS,CR
4 All
BL
HY,SI,SP,MD,CI,RS
BL
HY,BL,SI,MI,MD,CI
4 All
BL
4 All
BL
2 All
2 All
Time of
Sampling*5
January
March
July
May
July
April
August
March
July
March
July
June
June
a The nine study areas include Hylebos (HY), Blair (BL), Sitcum (SI), Milwaukee (MI),
St. Paul (SP), Middle (MD) and City (CI) Waterways, the Ruston-Pt. Defiance Shoreline
(RS), and Carr Inlet (CR).
b All sampling was conducted in 1984. The stations sampled in January were part of
the preliminary survey and the stations sampled in July were part of the Blair Waterway
Dredging Survey.
c At two of these stations, only conventional sediment variables were measured.
2.2
-------
COMMENCEMENT
BAY
HY-44
HY-39
HY-38
HY-31
NJ
•
00
HYLEBOS
WATERWAY HY-47
HY-46
HY-45
HY-18
CITY
WATERWAY
Locations of Commencement Bay stations sampled
for surficial sediment chemistry during March.
-------
• RS-22
• RS-24
fNJ
RS-21
RS-18
RS-19
RUSTON
N
0
I
J I
r
o
RS-20
COMMENCEMENT
BAY
4000
I I FEET
-| 1 METERS
1000
RS-13
TACOMA
RS-12
Figure 2.1. (Continued).
-------
en
STATIONS SAMPLED FOR SURFICIAL
SEDIMENT CHEMISTRY DURING JANUARY
STATIONS SAMPLED FOR SURFICIAL
SEDIMENT CHEMISTRY DURING JULY
COMMENCEMENT
BAY
Figure 2.2.
Locations of Commencement Bay stations sampled
for sediment chemistry during January and July
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-------
-RS-61
• RS-60
RUSTON
CO
N
o
I
• STATIONS SAMPLED FOR SUBSURFACE
SEDIMENT CHEMISTRY DURING MARCH
• STATIONS SAMPLED FOR SUBSURFACE
SEDIMENT CHEMISTRY DURING JULY
COMMENCEMENT
BAY
TACOMA
4000
J I FEET
1 METERS
1OOO
Figure 2.3. (Continued)
-------
HY-57
COMMENCEMENT
BAY
10
CI-56
cirr
WATERWAY
Figure 2.4. Locations of Commencement Bay stations sampled
for water column chemistry during April and
August.
-------
HY-50
COMMENCEMENT
BAY
STATIONS SAMPLED FOR BENTHOS
AND BIOASSAYS DURING MARCH
STATIONS SAMPLED FOR BENTHOS
AND BIOASSAYS DURING JULY
HY-44
HY-17
ro
•
t—i
o
CI-17
CITY
WATERWAY
Locations of Commencement Bay stations sampled
for benthic macroinvertebrates and sediment
bioassays during March and July.
-------
RS-22 (BIOASSAY ONLY)
ro
RS-24 (BIOASSAY ONLY)
BS-18
RUSTON
N
/t\
r
o
• RS-20
• RS-19
O 400O
I I I I I FEET
~~| METERS
10OO
• STATIONS SAMPLED FOR BENTHOS
AND BIOASSAYS DURING JANUARY
• STATIONS SAMPLED FOR BENTHOS
AND BIOASSAYS DURING JULY
COMMENCEMENT
BAY
RS-13
TACOMA
ns-12
Figure 2.5. (Continued).
-------
tvj
COMMENCEMENT
BAY
r
o
HY 70
N
/T\
4000
J I FEET
I
METERS
1000
Locations of Commencement Bay stations sampled
for fish histopathology and bioaccumulation
during June.
-------
^^^ RS 72
(S3
»
H-*
CO
RUSTON
N
0
I
I I
4000
I I FEET
r
0
METERS
TACOMA
COMMENCEMENT
BAY
1000
Figure 2.6. (Continued).
-------
• SURFICIAL SEDIMENT CHEMISTRY — JANUARY
SURFICIAL SEDIMENT CHEMISTRY, BENTHIC
MACROINVERTEBRATES, AND SEDIMENT
TOXICITY — MARCH
FISH HtSTOPATHOLOGY AND BIOACCUMULATION
JUNE
NOTE ONLY CONVENTIONAL SEDIMENT VARIABLES
WERE MEASURED AT CR-02 AND CR-05
Figure 2,7.
Locations of reference stations sampled in Carr
Inlet.
2.14
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TABLE 2.2. MEAN WATER DEPTHS BY STUDY AREA
FOR BENTHIC INFAUNA STATIONS
Study Area
Hylebos Waterway
Blair Waterway
Sitcum Waterway
Milwaukee Waterway
St. Paul Waterway
Middle Waterway
City Waterway (main
channel)
Wheel er-Osgood Waterway
Ruston-Pt. Defiance
Shoreline
Carr Inlet
Mean Lower
Low Water Depth
(ft)
30.09
37.2
39.7
35.2
12. 7b
18.0
24.1
6.1
26. OC
10.9
Standard
Deviation
(ft)
± 3-7
+ 3.2
+ 2.5
+ 2.3
+_3.6
±°
_+ 6.4
±°
+_5.0
+_5.1
Number of
Benthic Infauna
Stations
12a
11
3
3
4b
1
5
1
6C
3d
a Excludes Station HY-44 at a depth of 5.9 ft and excludes deepwater Station
HY-50 outside of Hylebos Waterway at a depth of 57.7 ft.
b Excludes Station SP-16 outside of waterway at 49.9 ft.
c Excludes Station RS-20 on transect away from the shoreline at a depth
of 67.2 ft.
d Excludes Station CR-12 at a depth of 62.2 ft.
2.15
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• Confirmation of potential reference sites and final selection
of specific sampling locations
• Initial QA/QC analyses, standardization of general cruise
protocols, and verification of field sampling methods
t Selection of contract laboratories and analytical protocols.
Final prioritization of areas and final selection of sampling stations
for the main part of the Commencement Bay project were dependent on the
elimination of data gaps through information collected in the January survey.
The January survey also allowed a better definition of the spatial extent
of known contaminated areas, and provided data on any "hot spots" that
potentially existed in areas not sampled previously.
After a review of historical information and data from the preliminary
survey, sediment stations were selected for the main part of the Commencement
Bay project conducted in March, 1984. The rationales for specific station
locations are presented in Tetra Tech (1984b). Briefly, stations were
selected for the following purposes:
• Filling data gaps
t Defining known areas of contamination more precisely
• Determining gradients of contamination in relation to suspected
sources.
Station locations were determined by line-of-site fixes on stationary
shoreline features. Photographic records were made of all position alignments
and ranges. These methods were tested and standardized during the preliminary
survey. Loran C navigation coordinates were also recorded for each station.
2.1.3 Data Analysis Methods
2.1.3.1 Chemical Contamination--
The magnitude and spatial extent of chemical contamination of sediments
was determined by comparisons of chemical concentrations among Commencement
Bay study areas and with reference conditions in Carr Inlet. Known and
blind replicate samples prepared from homogenized sediments were analyzed
as part of the quality assurance program to establish precision of laboratory
methods. Within-station variability was not evaluated. Therefore, tests
for statistically significant differences between Commencement Bay and
Carr Inlet that require within-station variability were not conducted.
Instead, sediment contamination was defined as "significant" if the concen-
trations in Commencement Bay sediments exceeded all reported values (or
detection limits) in any of up to nine Puget Sound reference areas, including
Carr Inlet.
Conditions in the nine reference areas were reported by several investi-
gators. Complete data for all chemicals studied in Commencement Bay were
available only for the Carr Inlet reference area. As a result of a check
2.16
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for anomalously high values in these reference areas, a single value for
phenol concentration [1,800 ug/kg dry weight (DW)] was excluded from one
Carr Inlet station when the significance of Commencement Bay sediment contam-
ination was determined. Data for 10 organic compounds in sediments from
one study of Samish Inlet and Dabob Bay were also excluded because detection
limits exceeded 50 ug/kg DW. These detection limits typically exceeded
observed values for these compounds in other reference areas, and were
substantially higher than detection limits obtained in the Commencement
Bay study.
Pearson linear correlation analyses and factor analyses (varimax rotation)
were performed for subsets of chemical data. Results were used to establish
relationships among the distributions of chemicals in Commencement Bay
study areas, and among sediment contamination, sediment toxicity, and benthic
infaunal abundances. Apparent effect thresholds derived for different
chemicals were established by comparing the range of concentrations for
each chemical in each of three groups of stations: 1) stations where^no
significant toxicity was observed, 2) stations where no significant depression
in benthic infaunal abundances was observed, and 3) stations where toxic
or benthic effects were observed.
2.1.3.2 Biological Effects--
To determine the potential biological effects of the observed chemical
contamination, each of four biological indicators (i.e., benthic macro-
invertebrates, sediment bioassays, fish histopathology, and bioaccumulation)
were compared between Commencement Bay and Carr Inlet. Although some compar-
isons were qualitative (i.e., descriptive), most were based on statistical
criteria. Use of such criteria ensured that impacts were judged objectively.
If possible, comparisons were made using parametric methods. Where the
assumption of parametric tests could not be met using either untransformed
or transformed data, nonparametric methods were used with untransformed
data. For each analysis involving multiple comparisons, the Bonferroni
inequality was used to achieve an experimentwise error rate of 0.05. This
method tests each comparison at a significance level equal to 0.05 divided
by the number of comparisons (i.e., comparisonwise error rate). By summing
all comparisonwise error rates, the significance level for the entire analysis
is 0.05. This method is simple but highly conservative (Snedecor and Cochran
1980). The specific statistical tests used for each biological indicator
are described below.
For benthic macroinvertebrates, number of taxa and number of individuals
were compared among study areas using the Kruskal-Wallis test. A posteriori
multiple range comparisons were made using the Mann-Whitney U-test. A
classification analysis was also conducted to group stations having similar
benthic invertebrate assemblages. This analysis used the Bray-Curtis Similarity
Index and the group average cluster strategy (see Boesch 1977) and was
conducted on the 64 most abundant taxa. Associations between abundances
of major taxa and the silt-clay content of bottom sediments were tested
using the product-moment correlation coefficient. Finally, log-transformed
abundances of major taxa at potentially impacted stations were compared
with abundances at reference stations using either the t-test or the approximate
t-test.
2.17
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For sediment bioassays, values of amphipod mortality and oyster larvae
abnormality were compared between potentially impacted stations and Carr
Inlet stations using either the t-test or the Mann-Whitney U-test. Results
of the two bioassays were compared with one another using Spearman's rank
correlation coefficient.
For fish histopathlogy, effects of sex and age on prevalences of hepatic
lesions were tested using a 2x2 contingency test and Spearman's rank correlation
coefficient, respectively. Age-normalized prevalences of hepatic lesions
were then compared between Commencement Bay areas and Carr Inlet using
2x2 contingency tests. Finally, weight-at-length values for fish having
lesions were compared with values for fish not having lesions using regression
analysis.
For bioaccumulation, tissue contaminant concentrations were compared
among study areas using the Kruskal-Wallis test. A posteriori multiple
comparisons were made using the Mann-Whitney U-test.
2.1.4 Geophysical Survey
Bottom and subbottom profiling was conducted throughout the waterways
of Commencement Bay to estimate the depth of accumulated sediments. The
scope of the subbottom data collection was limited to defining the soft/fluff
sediment accumulation layer that overlies either the natural bottom materials
exposed by dredging operations, granular fill materials placed by human
activities, or waste materials dumped or discharged into the waterways.
Bathymetric data were also collected to confirm the water depths recorded
on existing charts and to serve as a control for the concurrently collected
geophysical data.
The geophysical survey was conducted February 7-9, 1984. Horizontal
control was by means of a range-azimuth system. Azimuth was determined
by scaling off photo-montage maps, and range determined with a laser rangefinder
(Atlas Lara 90). Profiling devices used included a Raytheon Model 719B
200 kHz transducer system with a 7.5 degree beam width and a Ross Laboratories
Model 801 28 kHz transducer system with a 22 degree beam width.
Both acoustic profiling systems were "bar checked" prior to each day's
survey operations to set the water velocity calibration controls and draft
correction controls. The systems were also checked periodically during
the course of each day's operation. Time and location marks were recorded
on both recorder systems simultaneously. Data were transcribed from the
acoustic system records and entered into a computer for tide reduction
and final profile plotting of the data. Data were plotted with a DP-1
plotter to produce both length of waterway profiles and cross-waterway
profiles. A description of the data reduction procedures and a complete
set of the waterway profiles can be found in the "Commencement Bay Nearshore/
Tideflats Subbottom Profiling Task Report" (Raven Systems & Research, Inc.
1984).
2.2 SEDIMENT CHEMISTRY
Most chemical analyses were performed by U.S. EPA contract laboratories
following requirements under EPA IFB WA 83-A125 for trace metals and EPA
2.18
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IFB 84A-266 for trace organic compounds, with adjustments and additions
to the protocols specified under Special Analytical Services (SAS) contract
864-J.
2.2.1 Field Sampling
2.2.1.1 Surficial Sediment Samples--
Surf icial sediments for chemical analysis and bioassays were collected
using a 0.1-m2 modified van Veen bottom grab (galvanized steel) operated
in the normal manner. Because different tests were to be performed on
the sediments from different stations, the number of grab samples per station
varied from one to four.
Upon retrieval aboard ship, the exterior and interior of the grab
were checked for hazardous vapors using an HNu ionization detector prior
to any further handling. When vapors were detected (at low levels in the
worst case) or when a strong odor of f^S was present, protective breathing
apparatus was worn by all personnel near the sample.
To process the sample, the grab was placed in the metal sieving stand
used for the macroinvertebrates (Section 2.4). The upper flap of the grab
was opened and the contents examined to ensure that sufficient penetration
had been achieved and that no leakage or surface disturbance had occurred.
The grab was then carefully rocked to one side without disturbing the surface
layers and sufficient overlying water was decanted to expose the sediment
surface on the raised side of the grab. The upper 2 cm of sediment were
then removed using a glass plate as a spatula. No sediments near the sides
of the grab were collected.
The material removed from the grab was placed in either a glass jar
or in a large stainless steel bowl (the latter for large volumes) and carefully
homogenized by stirring with a stainless steel spoon. When color or textural
differences could no longer be detected, aliquots of the homogenized sediments
for chemical analysis were placed in glass jars with TFE cap liners (obtained
organically precleaned from the U.S. EPA sample management system), and
aliquots for bioassays were placed in new polyethylene bags. All sample
containers were closed, labeled, sealed with custody tape, and stored on
ice until returned to shore for shipment to the laboratories.
At 20 stations in Hylebos, Blair, Sitcum, St. Paul, and City Waterways,
samples were collected for analysis of volatile chemicals. At each of
these stations two 10-mL vials (VOA vials from U.S. EPA) were filled with
surface sediment using a stainless steel spatula to scrape surficial material
into the vials. This procedure was performed prior to collecting the upper
2 cm as described above.
Prior to sampling at each station, the grab was rinsed thoroughly
with site water and the glass plate, spoons, spatulas, bowl, and homogenizing
jars were rinsed in sequence with site water, pesticide-grade methanol,
and pesticide-grade dichloromethane, and finally wrapped or covered with
aluminum foil.
2.19
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2.2.1.2 Subsurface Sediment Samples--
Two coring devices were used during the subsurface sediment survey:
a standard gravity corer with a 10.2-cm steel barrel in lengths of 1.5
and 3.0 m, polycarbonate core liners, and 600 Ib of weight; and a box corer
with a stainless steel box approximately 25 x 38 cm in cross section.
Both devices were used at each sampling station to achieve maximum possible
undisturbed core length. The sample handling procedures for both devices
are described below.
Gravity Corer--As the corer was recovered from the water, the exterior
and inside the top were checked for hazardous vapors with the vapor detector
described previously. No vapor problems were ever detected at this point
in the sampling.
Upon recovery, the gravity core was carefully laid nearly horizontally
on the deck and the overlying water carefully decanted by tipping the cutter
end of the corer slightly above horizontal. The cutter and core catcher
were removed and the core liner pulled from the corer barrel. A 3.0-m
wooden trough was lined with aluminum foil. The deep end of the core liner
was then placed near one end of the trough and the liner was tapped gently
with a rubber mallet to dislodge the sediment from the liner. As the sediment
oozed out, the liner was moved along the trough to minimize distortion
of the core.
After extrusion, the entire length of the core was checked for hazardous
vapors. Core HY-63-G01 from off the salt pier at Occidental Chemical Corpora-
tion in Hylebos Waterway did have a significant response, and protective
breathing equipment was worn while processing that core. The outside of
the core was then scraped away with a stainless steel spatula and the core
was measured and examined. Total core length, and the depths of color,
odor, and textural horizons were recorded on field data logs. The core
was also photographed. Based on these observations, sampling horizons
were selected to provide adequate sample volumes and to obtain horizons
representative of any major discontinuities in the core. The sediments
between these horizons were then placed in a glass jar using a stainless
steel spatula. Care was taken to avoid collecting material that had been
in contact with the core liner or with the trough. The collected sediments
were homogenized and transferred to sample jars, as was done for the surface
sediments.
Between samples, the corer and core liner were washed with site water
and reassembled. The spatulas, homogenizing jars, and other tools were
rinsed with site water, solvent-washed, and covered with aluminum foil,
as was done during the surface sediment collections.
Box Corer--As the box corer was recovered from the water, it was checked
externally and internally for hazardous vapors, as before. No problems
were encountered. The flaps were then held open while the water overlying
the sediments was carefully removed using a small centrifugal pump. The
base plate was then attached, and the box was removed and placed in a wooden
rack at an angle of about 20 degrees from vertical. The side of the box
was carefully lowered to expose the vertical sediment face. All samples
were sufficiently cohesive that no slumpling occurred when the box was
2.20
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opened. Prior to further handling, the core was checked across the exposed
face for the presence of hazardous vapors.
The outer layer of the core was scraped away to expose the sediment
horizons. The total core depth and the depths of color and textural horizons
were recorded, and the core was photographed. As with the gravity core,
the horizons sampled for chemical analysis were based on these observations.
At the selected depths, a 10-cm wide glass plate was inserted horizontally
into the core. The overlying sediment was then cut from the box with a
stainless steel spatula and lifted with the glass plate to a glass jar.
The material was homogenized and aliquots prepared, as described above
for surface sediment.
Between stations, the box corer was rinsed with site water, while
the utensils were rinsed with water and solvent, as before.
2.2.2 Laboratory Analysis for Metals
Analyses were conducted for 16 elements, 13 of which are U.S. EPA
priority pollutant metals. Three of these "metals" (i.e., antimony, arsenic,
and selenium) are classified as metalloids, which are elements that do
not strictly occur as metals in the environment. Following U.S. EPA convention
and for ease of discussion, these three elements will be referred to as
metals.
Mercury determinations for all sediments were conducted with wet sediment
aliquots (0.5-g) digested using an aqua regia and KMn04/K2S20o mixture
and then analyzed by atomic absorption using the cold vapor technique (U.S. EPA
Method 245.5). Analyses of the remaining 12 U.S. EPA priority pollutant
metals plus barium, iron, and manganese were performed after drying the
samples at 50° C and digesting a 2-g aliquot with HN0.3 and 1^0? according
to methods detailed in the U.S. EPA Contract Lab Program IFB VIA 83-A125.
Digestates were taken to a range of final dilution volumes depending on
sample concentrations.
In the January sediment survey, chromium, iron, manganese, and zinc
were analyzed by flame atomic absorption; the remaining metals except barium
were analyzed by graphite furnace with Zeeman correction. Barium was not
analyzed for in the January survey. In the remaining surveys, barium,
beryllium, cadmium, chromium, copper, iron, manganese, nickel, lead, and
zinc were analyzed by Inductively Coupled Argon Plasma (ICAP). Silver,
arsenic, antimony, selenium, and thallium were analyzed by graphite furnace
with deuterium arc, background correction.
2.2.3 Laboratory Analysis for Organic Compounds
2.2.3.1 Volatile Organic Compounds --
Analyses for volatile organic compounds were conducted for 20 selected
surface sediment samples and one deep core sediment sample using 2-g to
5-g (wet weight) aliquots. Just prior to purging, 10 ml of organic-free
water spiked with three internal recovery standards (D4-l,2-dichloroethane,
bromofluorobenzene, and Ds-toluene) were added to the 40-mL VOA vial containing
the sample. After blending, the vials were connected to a Tekmar purge
2.21
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and trap instrument heated in a 60° c water bath, and the samples were
sparged onto traps containing 2:1 Tenax and silica.
Volatile compounds were desorbed at 180° C from the traps onto a 0.2
percent CW1500 stainless steel column (80-100 mesh, Carbopack C) held at
300 c. After desorption, the GC oven temperature was raised to 60° C and
held for 2 min, and then programmed at 8° C/min to 180° C and held for
19 min. A Finnigan 3100D with a Riber SADR data system was used for GC/MS
quantitation. Results were not corrected for recovery.
2.2.3.2 Semi-Volatile Organic Compounds--
Extraction and Cleanup—Prior to extraction, 100-g wet weight sediment
samples were spiked with 54 isotopically labelled recovery standards that
included 51 of the 56 U.S. EPA base/neutral/acid priority pollutants.
Samples were spiked with a total of 5 ug/component for base/neutral compounds
and 10 ug/component for acid compounds. This spike level resulted in an
absolute mass of 10-20 ng/component on-column for GC/MS analyses, assuming
100 percent recovery, and represented a tradeoff between spiking with enough
material to provide a reliable GC/MS signal and enabling the best determination
of detection limits at low levels for undetected compounds. Separate GC/MS
analyses of acid and base compound classes were not possible under the program.
Spiked sediments were Soxhlet-extracted in precleaned thimbles for
24 h using a 2:1 mixture of high-purity methylene chloridermethanol. An
intercomparison with a different extraction technique (i.e., direct sediment-
solvent contact under agitation) showed comparable results for most compounds.
Solvents were checked to ensure that they were contaminant-free prior to
use. All sediments were stirred during extraction to prevent channeling.
Sediments stirred easily after most of the water was removed in the initial
solvent cycles. Because of the substantial quantity of water removed from
the sediment during extraction, a water fractionation step was found to
be required. Water and methanol were removed from the sediment extracts
by partitioning against 50 percent Na2S04 saturated organic-free water,
maintained at pH <2 with 6N HC1 to prevent fractionation of acidic organic
compounds. Following isolation of the organic fraction, the aqueous wash
was adjusted to pH >12 with 6N NaOH, back-extracted with methylene chloride
to recover any basic organic compounds, and discarded. The combined organic
fractions were dried by passing the extract through a Na2SO-4 column and
reduced in volume to approximately 10 ml by gentle evaporation in a Kuderna-
Danish (K-D) apparatus.
Elemental sulfur was removed by shaking the extracts with 0.5 ml Hg
for at least 4 h. The desulfurized extracts were filtered to remove mercury
and salts, reduced to approximately 3 ml under a stream of purified No»
and subjected to gel permeation chromatography (GPC) using methylene chloride
as an eluant. GPC columns (20 mm x 300 mm) were slurry-packed with 19
g of Bio Beads S-X3 (Bio Rad) that had been equilibrated for 4 h with methylene
chloride, and were pressurized to 80 mm Hg (39 psi) with N?.
Each GPC column was calibrated using a 3-mL mixture of 200 mg/mL corn
oil, 4 mg/mL pentachlorophenol (PCP), and 4 mg/mL bis(2-ethylhexyl)phthalate
in methylene chloride. After the calibration mixture was charged to the
column, 5-mL aliquots of the eluant were collected and the amounts of PCP
2.22
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and phthalate were determined by gas chromatography using a flame ionization
detector (GC/FID). The amount of corn oil in each 5-mL aliquot was determined
gravimetrically. A plot of PCS, phthalate, and corn oil concentrations
in each 5-mL aliquot was then constructed and used to determine the elution
volume that maximized the removal of corn oil while minimizing the loss
of phthalate and PCP. For a typical sample, the first 40 ml of eluant
were discarded and the subsequent 100 ml were preserved.
Following 6PC cleanup, most sediment extracts were purified further
using disposable 3-mL solid phase extraction columns {SPE; Baker-10 Octadecyl).
Extracts from 6PC were concentrated to less than 6 mL by K-D, and then
to 1 mL using N£. A 10 percent (100 uL) aliquot was removed for PCB analysis.
The remaining extract was transferred to an 8-mL test tube with 3 mL of
methanol and reduced in volume to 1 mL using N£ to remove methylene chloride.
Each SPE column was conditioned with three column volumes of methanol prior
to adding the extracts and eluting with 7 mL of methanol. All used SPE
columns were archived. An excess of methylene chloride was then added
to the eluants and the mixtures were reduced in volume by K-D to approximately
1 mL, transferred to autoinjection vials, reduced to 0.5 mL using N£, and
submitted for GC/MS analysis. All GC/MS results were corrected for losses
during sample workup using the isotopically labeled recovery standards
spiked to each sample.
The 10 percent aliquots (100 uL) removed for PCB analysis were diluted
to 1 mL with hexane, charged to 3 g Alumina III (7 percent volume/weight)
in a 5-mL disposable pipet, and eluted with 11 mL of 20 percent methylene
chloride in hexane. The eluants were subsequently exchanged into isooctane,
adjusted to a final volume of 1 mL by K-D, and submitted for analysis by
gas chromatography/electron capture detection (GC/ECD).
Surface sediment samples from 55 of the 115 March sampling sites were
processed using silica gel chromatography instead of the SPE technique.
Tests using labelled recovery standards showed that equivalent recoveries
were obtained for most compounds using the two techniques, but that the
SPE technique enhanced recovery of phthalates and low molecular weight
chlorinated compounds such as dichlorobenzenes, hexachlorobenzene, and
hexachlorobutadiene. Because of this factor and the ease of analysis using
SPE chromatography, the SPE technique was used with all subsequent sediment,
particulate material, and tissue samples.
The 55 March surface sediment extracts processed by silica gel chromato-
graphy were subjected to acid/base partitioning after GPC cleanup in order
to isolate organic acids and bases that could be lost on silica gel. Silica
gel columns, topped with 2 cm of Na2S04, were prepared using 11 g silica
gel (EM Reagents, Kieselgel 60) that was activated at 1400 c and then slurried
in methylene chloride. After packing, all columns were rinsed with 40 mL
of pentane prior to loading the sample extract. Four eluants were collected
from the columns: (1) 22 mL pentane; (2) 44 mL of 3 percent methylene
chloride in pentane; (3) 44 mL of 1 percent methanol in methylene chloride;
and (4) 44 mL of 100 percent methanol. The first and last eluants, containing
aliphatic hydrocarbons and polar substances (e.g., pigments), were combined
and archived. The second eluant was diluted to 50 mL with hexane and a
10 percent aliquot (5 mL) was removed, concentrated to a final volume of
1 mL, and submitted for PCB analysis by GC/ECD. The remainder of the second
2.23
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eluant was then combined with the third eluant and the acid/base fractions,
concentrated to a final volume of 0.5 ml, and submitted for GC/MS analysis.
Surface sediments from the 17 sites sampled in January were subjected
to a more rigorous analysis using high pressure liquid chromatography (HPLC)
to separate chemically the extracts into three neutral fractions after
organic acids and bases had been isolated. Each of the five analytical
fractions was analyzed by GC/MS, and the fraction containing PCBs was also
analyzed by GC/ECD. The same mixture of isotopically labelled recovery-
standards used in later analyses was also used in this procedure. Recovery-
corrected results between this procedure and the simplified procedure used
for the majority of Commencement Bay organic chemical analyses were comparable
for most compounds. However, by removing sample interferences more effectively,
the HPLC procedure enabled an improvement of more than an order of magnitude
in detection limits (to less than 1 ug/kg dry weight). The reproducibility
of results for acid and base compounds was also improved by the separate
GC/MS analysis of these fractions.
GC/MS and GC/EC Procedures—Samples were analyzed using a Finnigan
GC/MS with an INCOS data system. Procedures were modified from U.S. EPA
1625 procedures for the isotope dilution technique (method of standard
additions) using mass spectrpscopy. The major change in the 1625 procedure
was that compounds for which there was no isotope analog were quantitated
by using the response factor of the nearest eluting, most chemically similar
labelled recovery standard. For example, benzo(g,h,i)perylene was used
for the quantitation of indeno(c,d)pyrene. When a chemically similar recovery
standard was not available (e.g., for tentatively identified compounds),
the response factor for the diQ-phenanthrene was used.
2.2.3.3 Total Extractable Organic Material--
The weight of solvent-extractable organic material was determined
for most sediments by determining the weight of the solvent-extracted residue
obtained from a 10-g (wet weight) sediment subsample shaken for 1 h with
1:1 methylene chlorideracetone. The resulting extract was filtered, reduced
in volume to approximately 5 ml by K-D, evaporated to dryness on a pre-
weighed aluminum dish, and weighed. The weight of any elemental sulfur
co-extracted with the organic matter was included in this determination.
2.2.4 Ancillary Analyses
2.2.4.1 Bulk Sediment Chemical Analyses--
Determinations of total organic carbon (TOC) and nitrogen (N) were
made for all sediments by combustion using either a Carlo Erba Elemental
Analyzer (January survey only) or a Perkin Elmer Elemental Analyzer. In
the January survey, total organic carbon was measured as the difference
between the total carbon content determined in combusted nonacidified sediments
and total carbonate determined separately by coulometric titration. Aliquots
of all subsequent samples were acidified to remove carbonate and organic
carbon was determined directly.
Total solids, total volatile solids (TVS), and oil and grease determina-
tions were made for all sediments according to procedures described by
2.24
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Plumb (1981). For percent solids, an approximate 25-g aliquot of well-
mixed wet sediment was transferred to a tared evaporating dish, weighed
to the nearest 10 mg, and dried overnight at 103-1050 C. The dried sample
was cooled, desiccated, and weighed to constant weight. The percent solids
was calculated based on the residue weight divided by the original sediment
wet weight.
TVS determinations were made by weighing the residue from the total
solids analysis after ignition at 550 ^50° C in a muffle furnace for a
minimum of 1 h. Volatile solids content was calculated based on the difference
between total solids residue and the volatile solids residue weights divided
by the total solids residue weight.
Oil and grease determinations were conducted with 10-g to 20-g aliquots
of wet sediment acidified with sulfuric acid to pH 2. MgSO^HpO was added
to the acidified sample to make a uniform paste. After solidification,
the sample was ground, added to a paper extraction thimble, and extracted
with Freon in a Soxhlet apparatus for 4 h. The resulting extract was distilled
using a water bath at 70° C, and the residue weight after removal of Freon
was recorded as total oil and grease content.
Sulfide was determined by titrating SAOB-buffered sediment samples
(20-g aliquot) with a standardized lead perchlorate solution and measuring
the endpoint with a specific ion electrode. Samples collected during the
January survey were immediately preserved in SAOB buffer upon receipt at
the laboratory, but subsequent samples analyzed by a different laboratory
were not buffered until analysis. Because holding times sometimes exceeded
30 days for these latter samples, total sulfide measurements were qualified
under QA review as minimum estimates. Sulfide levels in the January survey
samples showed a greater range in concentration than did the later samples.
2.2.4.2 Grain Size Analysis--
Sediment grain size was determined by sieve and pi pet analysis. After
dry and wet sieving of the gravel and sand fractions (-1 to 4 phi), the
remaining silt/clay fraction was treated with HgO? to remove organic material,
suspended in a settling column with a defloccufating agent, and sampled
over time according to procedures detailed by Folk (1974). The percent
weights of the gravel, sand, and silt fractions (-1 to 8 phi) were measured
for each 0.5-pni size interval. Percent weights for the clay fraction
were determined to the nearest 1.0 phi. Pipet sampling was discontinued
when the cumulative weight of the preceding phi size classes exceeded 95
percent of the total sample weight.
2.3 WATER COLUMN CHEMISTRY
2.3.1 Field Sampling
2.3.1.1 Metals—
In separate casts made at the stations and depths selected for organic
samples, samples for the analysis of particulate metals were collected
in standard 5-L PVC Scott Richards bottles. Upon retrieval aboard ship,
aliquots were collected from each bottle for salinity and oxygen using
2.25
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standard procedures. Then 1-gal polyethylene cubitainers were carefully
rinsed with the sample, filled, capped, and stored on ice until returned
to the laboratory. These samples were filtered through preweighed 0.4-um
Nuclepore filters, folded to protect the filtered material, and placed
in polycarbonate petri dishes. The dishes were sealed, labeled, and frozen
until shipped to the laboratory for reweighing and measurement of the trace
metals.
2.3.1.2 Organic Compounds--
Samples for the measurement of organic compounds in suspended particulates
were collected in 23-L stainless steel water bottles deployed at each of
two depths at each station: near the surface (0.5 m) and at 5 m. The
depths were selected to sample the brackish surface layer and the more
saline, deeper water. The adequacy of these depths was determined at the
start of each cruise by determining the depths of the thermocline and the
halocline with probes.
The sample bottles entered and exited the water with all ports closed.
The ports were opened only while sampling at the desired depth. Once sample
bottles were retrieved, two separate aliquots of 125-500 mL were collected
from each bottle and composited in polyethylene cubitainers. The remaining
water in the sample bottles was forced by nitrogen overpressure through
147-mm glass fiber filters held in either stainless steel or aged PVC filter
holders. (The filters were prepared by combustion at 500° C for 8 h followed
by solvent rinsing.) This sampling procedure was repeated with multiple
bottle casts until sufficient sample had been collected. In some cases
samples retrieved with the steel sampler were transferred to an aged PVC
pressure chamber for filtration.
While a minimum of 100 L was intended to be filtered for each sample,
the filters often clogged before this quantity could be forced through.
At different stations and depths, therefore, from two to eight sample bottles
were filtered and from one to four filters were used. When the entire
contents of a bottle could not be filtered, the volume of the remaining
water was measured and the volume filtered determined by difference.
After filtration, the glass fiber filters were removed from the filter
chambers with forceps, folded to protect the filtered material, and placed
in glass jars with TFE cap liners. The jars were labeled, sealed with
custody tape, and stored on ice until shipped to the laboratory for analysis.
The cubitainers of composited water were stored on ice until taken
to the laboratory for filtration. One of the duplicate aliquots from each
sample was filtered through a 0.45-um, preweighed Nuclepore filter, dried,
and reweighed for the determination of the dry mass concentration of the
sample. The other aliquot was filtered through a 0.4-um, combusted, silver
filter for determination of carbon and nitrogen content of the particulate
matter.
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2.3.2 Laboratory Analysis
2.3.2.1 Metals-
Polycarbonate filters (Nuclepore; 0.45-um pore size; 142-mrn diameter),
were used for metal participate filtration. After filtration, the filters
were dried at 60° c and weighed for total sample weight. The entire filter
was then placed in a beaker and the participates were digested using HNOo/H^
as for the sediments. The digestate was reduced to approximately 3 ml,
filtered, and then diluted to 10 ml. The standards used to calibrate the
April analyses were prepared using standard acid concentrations of 0.5
percent HN03. The standards used subsequently for the August survey were
matrix-matched in the same acid concentrations as the sample (approximately
20 percent HN03).
Because of the limited sample size, mercury analysis was omitted.
Analyses for barium, beryllium, cadmium, chromium, copper, iron, manganese,
nickel, lead, and zinc were performed by ICAP. Silver, arsenic, antimony,
selenium, and thallium were analyzed by graphite furnace atomic absorption
with deuterium arc background correction. If not detected by ICAP, cadmium
and lead were also analyzed by graphite furnace.
2.3.2.2 Semi-Volatile Organic Compounds--
Glass fiber filters containing particulate material were cut up into
Soxhlet thimbles using solvent-rinsed scissors and spiked with isotope
recovery standards at a level of 5 ug/component/sample. Procedural steps
for filters were identical to those for sediments taken through the SPE
chromatography protocol, except that the elemental sulfur removal and GPC
(Bio Beads) cleanup steps were omitted because the extracts were not complex.
The final dilution volume for the August particulate samples was reduced
to 0.05 ml from the 0.5 ml used for April particulate samples in order
to improve detection limits. The spike level was also lowered.
2.3.2.3 Ancillary Analyses—
The total organic carbon and nitrogen contents of particulate material
were based on 0.3-L to 1-L aliquots of site water filtered through 0.45-um
silver filters precombusted at 5500 c for 3 h. The sample aliquots were
taken from water collected for analyses of organic compounds. Organic
carbon and nitrogen measurements were made on the pelletized silver filters
using a Carlo Erba Elemental Analyzer. A set of standards and blank filters
was analyzed with each batch of samples in order to generate a multi-point
calibration curve. The calibration curves were used to determine appropriate
response factors for the range of concentrations observed in each sample
set (Hedges and Stern 1984).
A test was conducted to determine the amount, if any, of inorganic
carbon in the particulate material. Two filters from a group of replicates
were each cut approximately in half. One half was exposed to acid vapors
(Hedges and Stern 1984) and the other half was untreated. Based on the
lack of variation in atomic carbon-to-nitrogen ratios for the treated and
untreated samples, it was concluded that organic carbon was not present
in appreciable levels to warrant acid treatment of the samples.
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Suspended solids concentrations were determined for each water sample
collected for organic compound analyses by filtering a 1-L aliquot through
43-mm Nuclepore filters (Q.45-um pore size). The wet filters were rinsed
with distilled water to remove salts and dried to constant weight. Suspended
solid loads determined from these filters were used to estimate the total
particulate material on silver filters used in carbon and nitrogen determin-
ations, and on glass fiber filters used for organic compound analyses.
The dry weight of particulate material on Nuclepore filters analyzed for
metals was determined directly.
2.4 BENTHIC MACROINVERTEBRATES
2.4.1 Field Sampling
Sediment samples analyzed for benthic macroinvertebrates were collected
using a Q.06-m2 modified van Veen bottom grab. Four replicate samples
were collected at each of 54 stations. Forty-eight of these stations were
occupied in March, 1984 as part of the Superfund project. The remaining
six stations (all in Blair Waterway) were sampled in August, 1984 as part
of the Blair Waterway Dredging Study. Samples were sieved using mesh sizes
of 1.0 and 0.5 mm. All 1.0-mm fractions were analyzed taxonomically, whereas
all 0.5-mm fractions were stored for possible analysis in the future.
Upon retrieval, the grab was placed on a metal sieving stand for obser-
vation of sediment characteristics. The following characteristics were
recorded for each sample: sediment texture; sediment color; presence,
type, and strength of odors; penetration depth; degree of leakage or surface
disturbance; and presence of large animals or debris.
Samples displaying excessive leakage or surface disturbance were rejected.
Samples were also rejected if they did not meet the following minimum penetra-
tion depths:
• Coarse sand and gravel - 4 cm
t Coarse to medium sand - 5 cm
t Fine sand - 7 cm
• Silt with sand or clay - 10 cm.
Once sediment characteristics were recorded, the jaws of the sampler
were opened and the sediment was released into the top section of the sieving
stand. It was then gently sprayed with seawater as the larger masses of
sediment were broken apart. This material was rinsed into one of two stacked
screen boxes (1.0- and 5.0-mm mesh) in the lower level of the sieving stand,
where it was completely washed until materials no longer passed through
the screens. Material retained by each screen was transferred to thick
plastic bags labeled with external and internal tags. A 15 percent solution
of formalin buffered with sodium borate in seawater was used in the field
to fix the tissues of organisms.
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2.4.2 Laboratory Analysis
All 1.0-mm benthic samples were analyzed within 2-14 days following
collection. Each sample was transferred to a screening device with mesh
openings slightly smaller than those originally used in the field, and
the formalin was washed away using fresh water. The screened material
was transferred to a clean sample container having internal and external
labels, and the container was then filled with 70 percent ethanol solution.
Each sample was cataloged in a rescreening log, which was later compared
against field inventory notes to ensure that all samples were accounted
for. As mentioned earlier, all 0.5-mm benthic samples were archived for
possible analysis in the future.
Samples were sorted in one of two ways. Samples containing large
quantities of coarse material were processed using a flotation technique,
where the sediment was first rinsed in fresh water in a large, flat tray.
The organisms that became suspended in the water (soft-bodied organisms
and arthropods) were carefully poured into a sieve. This material was
sorted while viewing it through a binocular dissecting microscope at a
minimum of lOx power. The remaining portion of denser material was sorted
using a 5x hand lens. Organisms remaining in this portion generally consisted
of molluscs and some tube-dwelling or encrusting organisms associated with
the sediment grains. Samples containing less dense material were not processed
using the flotation technique, but were simply sorted under lOx magnification
using a binocular dissecting microscope.
Organisms were first sorted into major taxonomic groups: Annelida,
Arthropoda, Mollusca, Echinodermata, and other phyla. Quality control
of this sorting process was performed by resorting 20 percent of each sample.
Identification and enumeration of sorted organisms was to the lowest taxonomic
unit possible, generally to species level. This was accomplished using
dissecting and compound microscopes, the laboratory's taxonomic library,
and the laboratory's reference collection. Assurance of consistent identifi-
cations among individuals within the laboratory was accomplished by continuous
interaction of individuals, use of the reference collection, and use of
specially designed in-house taxonomic keys for difficult genera and species.
2.5 SEDIMENT BIOASSAYS
2.5.1 Field Sampling
Field collection methods for sediment bioassays are described in Section
2.2.1.1.
2.5.2 Laboratory Analysis
2.5.2.1 Amphipod Bioassays—
The infaunal amphipod Rhepoxynius abronius was collected subtidally
from West Beach on Whidbey Island (Washington) using a bottom dredge.
Amphipods were maintained and transported in clean coolers with ice, and
were returned to the laboratory within 18 h of collection.
2.29
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Following their arrival in the laboratory, amphipods were kept in
holding containers filled with fresh seawater (28 ppt salinity) and clean
sediment and maintained at 15+10 Q under continuous light until used in
testing. Cultures were aerated but not fed during acclimation and were
held for 4-14 days. Prior to testing, amphipods were sorted by hand from
sediments and identifications were confirmed using a Wild M5 dissecting
microscope. Damaged, dead, or unhealthy individuals were discarded.
Acute lethality of whole, fresh (unfrozen) sediments was measured
using the methodology of Swartz et al. (1982a, 1985), which involved a
10-day exposure to test sediments. A 2-cm layer of test sediment was placed
in 1-L glass jars and covered with 800 ml of clean seawater (28 ppt salinity).
Each beaker was seeded with 20 amphipods and aerated. Six replicates (20
amphipods each) were run per test sediment. Five beakers served to determine
toxicity, while the sixth beaker served as a reference for daily measurement
of water chemistry (i.e., pH, dissolved oxygen, salinity, and temperature).
Testing was conducted at 15+1° C under constant light. Test containers
were checked daily to estabVTsh early trends in mortality and sediment
avoidance, and also to gently sink any amphipods that had left the surface
overnight and become trapped by surface tension at the air/water interface.
A negative (clean) control sediment (from the amphipod collection site)
was run concurrently with each series of test sediments. In addition,
clean sediment spiked with CdCl2 to produce a concentration of 10 mg/L
was used as a positive control to ensure that response criteria (lethality)
were operative.
Amphipod dilution bioassays were conducted on samples from six stations
that were found to be highly toxic in initial tests. Dilution concentrations
were 100, 75, 50, 25, and 10 percent test sediment. Where insufficient
sediment was available for complete testing, replication was reduced and/or
the higher test sediment concentrations (100 and 75 percent) were eliminated.
Sediment dilutions were determined gravimetrically using a 2-cm layer of
100 percent test sediment as a standard upon which to base the remaining
concentrations of that sample. Sand from West Beach on Whidbey Island
was mixed with the test sediment to attain homogeneous sediment dilution
weight equivalent to that of the 100 percent sample.
Bioassay tests were terminated after 10 days, when sediments were
sieved (0.5-mm screen), and live and dead amphipods were removed and counted.
Amphipods were considered dead when there was no response to physical stimu-
lation and microscopic examination revealed no evidence of pleopod or other
movement. Missing amphipods were assumed to have died and decomposed prior
to the termination of the bioassay (Swartz et al. 1982, 1985).
2.5.2.2. Oyster Larvae Bioassays--
Adult Pacific oysters (Crasspstrea gigas, age 3-5 yr) were obtained
from Baynes Sound Oyster, a commercial oyster farm located in Union Bay,
British Columbia. Prior to testing, the oysters were cleaned of fouling
organisms and placed in continuous-flow conditioning trays to permit gonadal
maturation. The oysters were thermally conditioned (19+1° C) for 4-6 wk
in unfiltered seawater, with individual oysters periodically sacrificed
to determine the state of gonadal development.
2.30
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Spawning was induced by thermal stimulation and the addition of a
prepared sperm suspension from a sacrificed male oyster, following standard
procedures described in Chapman et al. (1983, 1984), Chapman and Morgan
(1983), and ASTM (1983). The fertilized eggs were washed through a Nitex
screen (0.25-mm mesh size) to remove excess gonadal tissue and were then
suspended in 4 L of filtered (0.45 urn nominal pore size), UV-treated seawater
at incubating temperature. When microscopic examination revealed the formation
of polar bodies, egg density was determined from triplicate counts of the
number of eggs in 1-mL samples of a 1:99 dilution of homogeneous egg suspension.
^Sediment bioassays were conducted in clean (rinsed with 5 percent
nitric acid) 1-L plastic bottles. Fifteen grams (wet weight) of the appropriate
sediment was added to each bottle and the volume brought up to 750 ml with
treated seawater to make a final concentration in all test containers of
20 g (wet weight) of sediment per L of seawater. Two seawater and two
sediment controls contained 20 g/L of clean sediment, collected from off
West Beach, Whidbey Island. One seawater and one sediment control were
spiked with CdCl2 to produce a concentration of 10 mg/L and served as positive
controls for 100 percent lethality [Martin et al. (1981) reported a 48-h
EC50 of 0.61 mg/L Cd for Pacific oyster larvae]. All test sediments were
run in duplicate and the controls were replicated five times.
Dilution bioassays were conducted on samples from five stations that
were found to be highly toxic in initial tests. Concentrations of test
sediments used in the dilution bioassays were 20, 15, 10, 5, and 2 g/L,
with the remaining volume (to make up a 20-g/L concentration) provided
by clean control sediment. Seawater and clean sediment controls were prepared
and run in duplicate.
The sediments were suspended by vigorous shaking for 5 sec. Embryos
were then added and the suspended sediments were allowed to settle. No
additional agitation was provided after inoculation.
Within 2 h of fertilization, each container was inoculated with approxi-
mately 22,000 developing oyster embryos, to give an approximate concentration
of 30 per ml. The containers were covered and air-incubated for 48 h at
20+10 c. After 48 h, larvae were concentrated using a 0.038-mm sieve,
Quantitatively transferred to screw-cap glass vials, and preserved with
percent buffered formalin. Preserved samples were examined in Sedgewick-
Rafter cells under lOOx magnification. Because bivalve larvae sink after
preservation (ASTM 1983), it was possible to discard most of the water
(70 percent) from the sample vials before examining the residual volume
containing the larvae.
Normal and abnormal larvae were enumerated to determine percent survival
and percent abnormality. Percent survival was determined as the number
of larvae surviving in each test container relative to the seawater control.
Larvae that failed to transform to the fully shelled, hinged, "D-shaped"
prodissoconch I stage were considered abnormal. The results of the dilution
bioassay were also analyzed to estimate the 48-h median effective concentration
(EC50) based on abnormal shell development.
Salinity, dissolved oxygen, and pH levels were initially adjusted
in each container to 28 ppt, 7.6-7.8 mg/L, and 7.9-8.0, respectively.
2.31
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These variables were measured for each container at the termination of
the bioassays.
2.6 FISH HISTOPATHOLOGY
2.6.1 Field Sampling
Demersal fish assemblages in Commencement Bay and Carr Inlet were
sampled June 4-9, 1984 aboard the RV KITTIWAKE. Fishes were collected
using a 7.6-m (headrope) Marinovich otter trawl, having a body mesh size
of 3.2 cm (stretched) and a cod-end liner mesh size of 1.3 cm. All trawling
was conducted at a constant vessel speed of approximately 2.5 kn during
daylight hours (i.e., 0630-1700).
English sole (Parophrys vetulus) larger than 225 mm total length (TL)
were targeted for histopathological analysis. Larger fish were selected
for analysis because Malins et al. (1982) found that lesion prevalences
in English sole less than 2 yr old were substantially lower than prevalences
in older fish. The present study therefore focused on fish most likely
to be afflicted with liver disorders (i.e., fish >_ 3 yr old).
At each of the 17 trawl transects, all target fish were removed from
the total catch and pooled in a large bucket. Sixty individuals were then
randomly selected for analysis, yielding 1,020 fish for the entire study.
Each selected fish was sacrificed by a blow to the head, weighed (nearest
g wet weight), measured (nearest mm TL), examined for grossly visible external
abnormalities (e.g., lesions, scoliosis, fin erosion, parasites), and tagged
with a code number. Following external examination, each fish was transferred
to the shipboard laboratory for internal examination and liver removal.
In the laboratory, the abdominal cavity of each specimen was surgically
opened to reveal the visceral organs. After all internal organs were inspected
for the presence of grossly visible defects, the liver was removed in its
entirety and placed on a stainless steel plate. With the use of stainless
steel dissecting tools, the liver was cut into multiple sections and examined
for the presence of lesions. The color of the organ was noted, a portion
of the tissue was placed in 10 percent neutral buffered formalin for subsequent
histopathological analysis, and the remainder of the liver was placed in
vials and frozen for later chemical analysis. If hepatic lesions or discon-
tinuities were noted, the section for histopathological examination was
taken from the affected area. If the organ appeared to be normal, the
section for histopathological examination was taken from the center of
the liver at its broadest point. Following removal and dissection of the
liver, the gonads were inspected and the sex of the fish was noted. The
head was then removed, a tag bearing the accession number of the fish was
placed in the left opercular chamber, and the head was frozen for subsequent
age determination by otolith examination.
All fishes in the remainder of the catch at each station were identified
to species and counted. All English sole not selected for histopathological
analysis were measured (nearest mm TL) and counted.
2.32
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2.6.2 Histopathological Examination
Each formalin-fixed liver sample was dehydrated in a graded series
of ethanol, cleared in xylene, and embedded in paraffin. Two 4-um sections
were made using a rotary microtome. One section was stained with hematoxylin
and eosin. The remaining section was left unstained for possible future
use.
Prepared slides were examined using conventional light microscopy.
All observed abnormal conditions were verified by Mr. Mark Myers, the chief
pathologist of the Environmental Conservation Division of the Northwest
and Alaska Fisheries Center of the National Marine Fisheries Service (NMFS).
This verification procedure ensured that results of the present study are
comparable with those of past studies conducted in Puget Sound by the NMFS
Environmental Conservation Division (e.g., Malins et al. 1980, 1982, 1984).
2.7 BIOACCUMULATION
2.7.1 Field Sampling
2.7.1.1 Specimen Collection--
Bioaccumulation analyses were conducted on English sole and cancrid
crabs. Because of its economic importance, the Dungeness crab (Cancer
magister) was the preferred invertebrate species. However, two confamilial
species (i.e., £. productus and £. gracil is) were retained for possible
analysis because it was uncertain whether adequate sample sizes of C. magister
could be obtained at every station.
At each study site, five English sole were randomly selected from
the 60 fish used for histopathological analysis (see Section 2.6). Each
fish (whole body minus liver and head) was tagged with a code number, wrapped
in aluminum foil, stored on ice, and returned to the shore-based laboratory
for tissue removal.
Cancrid crabs were collected from the trawl catches at each study
site. Crab pots were also fished near each trawl transect to provide additional
specimens. Each crab (whole body) was tagged, placed in a polyethylene
bag, held live on ice, and returned to the shore-based laboratory for tissue
removal.
2.7.1.2 Tissue Removal--
English Sole—Each fish was first rinsed with tap water to remove
any adherent contaminants and then scraped with a stainless steel spatula
to remove surface mucus. The carcass was then placed on an absorbent pad
and the upper fillet was removed with the skin intact. The carcass was
then turned over and the opposite fillet was removed. Both fillets were
placed skin-side down on a precleaned glass plate and the skin was removed
using a stainless steel filleting knife. The skinned fillet was then cut
into 6-g and 36-g portions, which were stored frozen in glass bottles for
subsequent metal and organic analyses, respectively.
2.33
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All instruments were stainless steel and were cleaned between use
on each fish. The cleaning procedure consisted of washing with tap water
to remove any adherent tissue, wiping clean with a sterile gauze pad, soaking
in methylene chloride (nanograde), and finally rinsing with double-distilled,
deionized water (tissue culture quality). Work surfaces were washed with
95 percent ethanol, followed by methylene chloride. With the exception
of the external skin surface, each fish was handled with cleaned stainless
steel instruments and came into contact with precleaned glass only.
To ensure that samples were not mixed, each specimen was identified
and processed to completion before a second animal was started. This consisted
of removing the identifying label that accompanied the carcass, labeling
the final collection jars, and processing the entire specimen before beginning
the next. The original identification tag accompanied the sample from
the carcass to the final sample jar. All specimens from each collection
site were stored as a group to ensure that specimens from different study
sites were not mixed.
Cancrid Crabs—Each crab was first washed with tap water to remove
surface contaminants and then dried using a paper towel. All legs were
cracked off at the body suture and placed on a precleaned glass surface.
Muscle tissue remaining inside the body was removed using curved stainless
steel forceps and placed on the glass surface. The end of each leg was
then cut with scissors and the muscle tissue was expressed by squeezing
from one end of the leg toward the cut end. This tissue was added to the
body tissue, mixed thoroughly, divided into 6-g and 36-g portions, and
stored frozen in glass bottles for later metal and organic analyses, respec-
tively.
All instruments and work surfaces were treated using the same procedures
as those described previously for fish tissue removal. In addition, all
crabs from each study site were processed individually and stored as a
group to ensure that specimens from different study sites were not mixed.
2.7.2 Laboratory Analysis for Metals
2.7.2.1 Muscle tissue—
For the first set of muscle tissue analyses, a 2-g aliquot of wet
tissue was used for analyses. The tissue was held overnight in HNO-3, then
digested as for metals, and the digestate was diluted to 100 ml. Barium,
beryllium, chromium, cobalt, copper, iron, manganese, nickel, silver, and
zinc were analyzed by ICAP. Arsenic, cadmium, lead, antimony, selenium,
and thallium were analyzed by graphite furnace with deuterium arc background
correction. Mercury was analyzed on a separate 0.5-g aliquot using cold
vapor atomic absorption.
Subsequent QA review of the data indicated that the aforementioned
protocol had not been followed for the tissue analyses except for the mercury
determinations. Consequently, many elements were not detected, and the
detection limits reported were not as low as originally requested. Thus,
reanalysis of the muscle tissue was required. Due to limited sample size,
cadmium, chromium, copper, lead, nickel, and silver as elements of critical
importance were requested for reanalysis. No tissue remained for one sample
2.34
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(HY-71-560), and the remaining sample quantities varied from 0.38 g to
8.05 g wet weight. To obtain total solids measurements, the entire remaining
sample was dried at 50° C prior to HNOWH20£ digestion. The entire aliquot
of dried tissue was digested using similar procedures as for the sediments.
The resulting digestates were diluted prior to analysis such that the maximum
dilution factor, based on sample weight, was 12.5. Analyses for chromium,
copper, and nickel were performed by ICAP. Cadmium, lead and silver were
analyzed by graphite furnace AA with deuterium arc background correction.
2.7.2.2 Fish Livers--
Approximately 0.5 g (wet weight) of liver tissue was digested using
persulfate and analyzed for Hg using the cold vapor technique. The remaining
liver tissue, consisting of samples sizes ranging from 1.04 g to 9.14 g,
was dried at 60° C to obtain percent solids content and then digested using
HN03 and H202- The digestates were diluted to 25 ml if less than 2 g was
digested, or to 50 ml if more than 2 g was digested. Iron and zinc were
analyzed for by flame atomic absorption. All other metals were analyzed
by graphite furnace with Zeeman correction.
2.7.3 Laboratory Analysis for Organic Compounds
2.7.3.1 Volatile Organic Compounds--
Volatile organic compound analyses were conducted for 20 selected
fish tissue samples using 1-g tissue aliquots blended with 3 ml of organic-
free water and spiked with three recovery standards. The blended samples
were transferred back into VOA vials and the tissue blender was rinsed
twice with additional 3-mL aliquots of organic-free water. After addition
of internal standards, the sample was analyzed according to the purge and
trap technique described for sediments.
2.7.3.2 Semi-Volatile Organic Compounds--
Homogenized muscle and liver tissue samples were mixed with approximately
30 g Na2$04 in a beaker prior to adding to precleaned Soxhlet thimbles
for extraction. When possible, approximately 25 g of wet muscle tissue
was used for analysis; some individual fish and most crab samples had less
material (a minimum of 13 g wet weight crab muscle). Because of the limited
mass of individual fish livers (1.5-3 g wet weight), liver tissue was composited
from 6-40 fish (in samples used for replicate analyses) to yield 6-25 g
wet weight for organic analyses. The same total amount of labelled recovery
standards used to spike sediments (5 ug/component/sample) was also used
for tissues. Although this amount resulted in a higher spike level (>400
ug/kg wet weight) than that used with sediments because less tissue sample
was available, the same final dilution volume was required.
Fish and crab muscle tissue Soxhlet extracts were partitioned against
acidified organic-free water as described for sediment extracts. Because
of the simplicity of the extracts, the elemental sulfur removal step and
SPE chromatography step used with sediments were omitted for tissues.
GPC cleanup (Bio Beads) was required because of the high lipid content
of the tissues, and was performed as described for sediments. All tissue
extracts to be analyzed by GC/MS were taken to a final dilution volume
2.35
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of 0.5 ml following GPC; a one-tenth aliquot for PCB analysis by GC/ECD
was taken to a final volume of 1 ml.
2.7.3.3 Total Extractable Organic Material--
The weight of solvent-extractable organic material in tissues was
determined directly from the same extract used for chemical analyses.
After allowing the Soxhlet extracts to settle overnight, a 1-mL aliquot
was transferred to a pre-weighed aluminum dish, evaporated, and weighed.
This aliquot was typically 1/200 of the total extract. The weight measurement
of a smaller aliquot was not feasible because an electrobalance was not
available for this analysis.
2.8 DATA MANAGEMENT
As part of the overall management support provided to WDOE, a data
management system was developed for the Commencement Bay Nearshore/Tideflats
Remedial Investigation. The system was designed to manage the large quantities
of data that were collected and used for this investigation and to provide
WDOE with a tool for long-term management of environmental data frcm Commence-
ment Bay.
The data management system consists of a central database, additional
data analysis capabilities, and a library. It was developed using an IBM
microcomputer and the Knowledge Man relational database software package.
2.8.1 The Database
The Commencement Bay database consists of 23 data files, each storing
a different type of data. Data of different types are linked by common
identifiers. There are two sets of key identifiers: survey-station-sample
and drainage. All data are identified by survey or research project, by
a carefully located station, and by a description of the sample that was
taken for analysis. In addition, data are identified by location within
the Commencement Bay drainage system defined and described for this project
(i.e., along a waterway, ditch, pipe, drain, or seep).
These two sets of identifiers make it possible to examine data from
several points of view. Different data sets that are related in space
and/or time can be retrieved easily in a form that enables comparison.
For example, drainage identifiers can be used to retrieve all data for
a given point source or to plot spatial changes in a variable (e.g., chemical
concentration) along a creek, ditch, or aquifer. These latter capabilities
were used extensively during the project for source identification.
Currently, the Commencement Bay database contains over 25,000 records,
each consisting of 15-150 separate parameters. There are descriptions
of over 50 surveys, 500 sampling stations, and 2,000 samples of water,
solids, and biota. More than 400 components of the Commencement Bay drainage
system have been identified. Types of data stored include inorganic and
organic chemicals; conventional variables for both sediment and water;
results of amphipod, oyster larvae, and bacterial bioassays; and observations
on fish pathology and benthic community structure.
2.36
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The large quantity of data is easily managed within the menu-driven
system, which allows access to all files. The menus enable the user to
enter, edit, view, report, or process data of any data type by simply typing
one to three letters at each choice. Data from a particular station or
sample can be retrieved quickly and viewed by selecting two or three descrip-
tors.
2.8.2 Data Analysis
Standard reports are built into the menu-driven system. Reports can
be simple or complex tables, forms, spreadsheets, or graphics. Reports
are available to provide simple statistics and to calculate mass loadings.
For non-standard, one-time requests, the database software contains a special
"structured language" very close to English that allows a user to request
needed information.
For more complex analyses, data retrieved via the menu-driven reports
or ad-hoc queries can be written to a file in standard ASCII format. These
retrievals can then be included in word-processed reports; used with other
analysis programs, statistical packages, or models; or transferred to other
computers via modem.
Data analyses conducted to apply decision criteria and to identify
contaminant sources for Commencement Bay involved the use of the database
and several auxiliary packages. The database was used to retrieve partial
and entire data sets and to calculate statistics such as means and detection
frequencies for chemical compounds, mean mortalities of bioassay organisms
by station and by waterway, and counts of the number of fish with lesions
of certain types. For source identification, the ability to search for
data on the basis of drainage enabled retrievals of all historical data
for a certain pipe or all data on a certain compound from a set of discharges
to a waterway.
Data were also transferred via file to the SPSS/PC software package
available for IBM microcomputers. This package was used extensively in
running parametric and nonparametric statistical analyses (e.g., correlations,
analyses of variance, t-tests, and factor analyses) as well as in calculating
elevations above reference. Data were transferred to SPSS on a Prime mini-
computer for performing cluster analyses, and several Fortran programs
were used for other analyses.
2.8.3 Graphics
The LOTUS 1-2-3 spreadsheet was used to create graphics to display
data. Spatial information stored for stations in the database enabled
any data point to be placed at a position along a drainage. The spreadsheet
was used to graph the concentration of a given contaminant against distance
from the mouth of the waterway or drainage. In addition, the shoreline
of Commencement Bay was digitized and the coordinates incorporated into
spreadsheets. Maps of the area were then created. The scale of these
maps can be adjusted and actual data values can be graphically presented
on these maps.
2.37
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2.8.4 Data Quality Control
Extensive quality control procedures were used in coding and entering
data. All historical data considered for inclusion in the database were
evaluated by technical personnel. All new data collected for the project
were subjected to extensive quality assurance (QA) by technical personnel.
Throughout the data-screening, coding, and entry process, data personnel
worked closely with technical staff in properly coding data and qualifying
data as indicated by QA review.
Data were entered into the database using forms identical to those
used for coding. Extensive error trapping facilities were used, including
a set of programs to check the entered data for errors in identifiers or
codes. One hundred percent of all data collected to analyze sources and
levels of contamination in Commencement Bay were verified after entry.
The database was designed to provide information about data quality
and data interpretation along with the actual data. Data are referenced
to the document containing the original data. This allows a user to return
to the original source if desired. The initials and organization of the
QA officer who reviewed the data are also stored. Codes for each particular
analysis method are also stored so that later retrieval of data for a particular
use could specify use of data analyzed by certain methods only.
2.8.5 Library
A Commencement Bay project library was established which contains
over 500 pertinent documents, including technical and administrative reports,
correspondence, maps, and references. A complete copy of all documents
in the library is located in the WDOE Project Office in Olympia and at
Tetra Tech's office in Bellevue. Documents are filed by accession number.
This information is linked to the database in an overall records and
document management system. A file in the database stores information
on the documents in the project library by their accession number. It
is possible to search for documents by number, title, author, agency, any
word in the title, and by subject area. All data within the database are
referenced to a document, enabling a user to easily locate original sources
if needed.
2.9 HEALTH AND SAFETY
A site-specific safety plan (Brown and Caldwell and E.V.S. Consultants
1983) was prepared for the data collection and field operations conducted
under Tasks 3 and 4 of the Commencement Bay Nearshore/Tideflats Remedial
Investigation. The safety plan was based on guidelines in Tetra Tech (1983b).
Both plans were approved by the WDOE Project Manager and the U.S. EPA Region
X Safety Officer.
Procedures described in the site-specific safety plan ensured safe
collection of data of adequate quality to meet contract specifications.
The plan specifically called for a modified Level D protection with the
substitution of marine rubber work boots with non-slip soles for steel-toed
boots. Monitoring equipment included an HNu photoionization detector and
2.38
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personnel organic monitoring badges. Collection of certain deep core and
sediment samples required the use of respirators with GM C-H combination
cartridges for acids, gases, and organic vapors (MSA 464 046). The site-
specific safety plan includes the following sections:
Introduction
Site safety plan summary, Tasks 3 and 4
Site description
History of site activities
Contractor's site safety work plan
Hazard evaluation and potential chemical exposure
Key personnel
Work effort and levels of protection
Designated work areas
Personnel and equipment
Site emergency procedures
Emergency facilities
Monitoring of air and personnel
Personnel training
Weather and other conditions which may affect site operations
Access by unauthorized personnel
Decontamination
References.
2.10 SAMPLING AND ANALYSIS QA/QC
QA/QC procedures applied in the Commencement Bay Nearshore/Tideflats
Superfund Investigation were geared to cover interdisciplinary field sampling,
laboratory analyses, and data analysis/validation of over a million data
values on approximately 28,000 data records. Specific procedures used
in each of these areas were summarized in a QA/QC project plan approved
by the U.S. EPA and WDOE (Brown and Caldwell and E.V.S. Consultants 1984).
These procedures covered necessary collections of water, biota (fish and
crab species), surface and subsurface sediments, and suspended particulate
material for analyses in organic and inorganic chemistry, benthic ecology,
sediment toxicology, and fish pathology.
Results from analytical laboratories were reviewed by Tetra Tech for
conformance with QA/QC requirements and to resolve analytical problems.
Detection limits, recovery, precision, completeness, and conformance with
the specified protocol were verified during data review. Ten to twenty
percent of the data was examined in a complete verification effort. The
remainder of the data was evaluated for outliers and completeness prior
to submission for database entry. All of the spectral data for the tentatively
identified organic compounds were manually examined. When possible, QA
audits included the use of known geochemical trends in environmental data
to evaluate the reliability of the data returned for interpretation.
2.10.1 Sample Collection
Integration of field tasks and study results was accomplished by estab-
lishing common sampling sites, sampling methods, and sampling times for
related disciplines, as specified in the project sampling and analysis
plan (Tetra Tech 1984b). Field sampling procedures included instructions
2.39
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for navigation, geophysical investigations (bottom profiling), use of field
sampling gear, sample container preparation, sample preservation and holding
times, and shipping procedures. Special sample handling requirements to
ensure the integrity of samples were also defined, for example, the need
to exclude air spaces in the collection of sediments for volatile organics
analysis. Sample alteration checklists were used to document authorized
changes in previously established procedures in order to provide an accurate
record for use in data interpretation. Sample custody records were maintained
so that sample possession could be traced from the time of collection to
the time of introduction as evidence in enforcement proceedings. Replicate
archive samples of all sediment samples collected for analysis, and unanalyzed
fish liver samples were maintained in freezers should additional analyses
be warranted in the future. Selected formalin-preserved benthic taxonomy
samples were retained to document a reference collection.
2.10.2 Organic Compound Analyses
A method validation study involving four laboratories was conducted
to evaluate established analytical protocols of varying sophistication
used for the determination of trace organic compounds in sediments. Based
on the QA evaluation of these data, a modified protocol was recommended
by Tetra Tech for use in the project in coordination with requirements
of the U.S. EPA Contract Lab Program (CLP). The method of standard additions
used in this protocol (the isotope dilution technique using 54 labelled
recovery standards) enabled the correction for target compound losses during
sample workup. Validation of this modified chemical protocol was accomplished
by a step-wise verification of compound recoveries during each stage of
the protocol before sample processing began. Recoveries of >80 percent
for each stage were required and attained for almost all compounds in tests
with spiked blanks.
The contract laboratory performing these analyses followed routine
QC guidelines defined by the CLP and include:
• Documentation of GC/MS mass calibration and abundance pattern
• Documentation of GC/MS response factor stability
• Internal standard response and retention time monitoring
• Reagent blank analysis
• Surrogate spike response monitoring
• Matrix spike and duplicate analysis (one each per 20 samples).
Specific procedures regarding the laboratory performance requirements
are stated in the IFB WA 84A-266 contract and in special analytical services
(SAS) contract 864J. Additional quality control checks included analysis
of "blind" replicates for sediment and biological tissue. Because of the
small sample size, no "blind" replicates or matrix spikes were performed
on the particulate filters. A summary of available data on precision of
recovery-corrected concentrations in different samples and the recovery
of isotopically labeled recovery standards spiked in each sample is provided
2.40
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in Table 2.3. Precision of the recovery-corrected values was calculated
only when compounds were detected in samples. Not all chemicals were detected
in each set of replicate samples.
A list of tentatively identified compounds was compiled from detailed
analysis of 17 preliminary samples. The compounds were specifically "searched"
for in all the sample extracts. All the spectral data for these compounds
were manually examined.
2.10.3 Trace Metals and Ancillary Analyses
The laboratories performing these analyses followed routine QC guidelines
defined by the U.S. EPA contract laboratory program and include:
• Documentation of initial and continuing calibration for each
metal
• Documentation of instrument detection limits
• Procedural blank analysis
• Matrix spike and duplicate analysis (one each per 20 samples).
Specific procedures regarding the laboratory performance requirements
are stated in the IFB WA83-A125 contract and special analytical services
contract 864J. Additional quality control checks included the analysis
of "blind" replicates for sediment and biological tissue. Duplicate blind
replicates and matrix spikes were not performed on the filters due to the
limited sample size. The National Bureau of Standards standard reference
material (SRM) bovine liver was submitted for analysis with the fish livers.
Oyster tissue SRM was submitted with fish tissue. A summary of available
precision and recovery data is provided in Table 2.4. The results of the
analysis of the bovine liver SRM caused the values for arsenic and lead
in fish liver to be qualified as questionable.
The precision of ancillary sediment data accepted was within QA require-
ments as demonstrated by replicate analyses for percent solids (mean ±
2.7 RPD), volatile solids (mean +. 2.3 RPD), total organic carbon (mean
± 5.6 RPD), and nitrogen (mean ± 3.6 RPD). Sulfide and oil and grease
analyses showed greater variability with ± 39 RPD and ± 30 RPD, respectively.
Sulfide results are used only as a semi-quantitative measurement in these
reports because of lab holding time and preservation problems.
2.10.4 Benthic Macroinvertebrates, Sediment Bioassays, and Fish Histopathology
The QA procedures for these analyses are described in Sections 2.4,
2.5, and 2.6.
2.11 RISK ASSESSMENT
"Risk assessment" is a descriptive term applied to an analysis of
hazard potential in an environment. All risk assessments have two elements
in common:
2.41
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TABLE 2.4. SUMMARY OF AVAILABLE PRECISION AND RECOVERY DATA
FOR COMMENCEMENT BAY INORGANIC CHEMISTRY SAMPLES
Precision (Mean RPDja
Percent Recovery
Antimony
Arsenic
Barium
Beryl lium
Cadmium
Chromium
Copper
Lead
Iron
Manganese
Mercury
Nickel
Selenium
Silver
Thai lium
Zinc
Surface
Sediment
+ 14
+ 8.1
+ 3.3
+ 2.4
+ 4.7
+ 6.3
+ 5.0
+ 5.5
T2.4
+ 2.7
T 8.2
+. 8.5
-
+ 17
+" 0
+ 36
English
Muscle
_
+_ 24
-
-
-
-
-
-
-
+ 7.6
I 12
-
+_ 38
-
-
^7.0
Sole
Livers
_
+ 35
^46
-
+ 12
+ 29
T12
+ 56
+ 11
+ 7.3
T 5.6
T32
T62
+ 32
T 20
+ 20
Surface
Sedimentb
92
89
99
99
97
99
98
100
-
100
100
98
79
90
87
100
English
Muscle0
_
-
-
-
87
90
100
115
-
-
-
84
-
100
-
-
Sole
Livers^
_
3606
-
-
140
-
90
450e
100
-
-
-
_
_
-
64
a Precision determined by multiple sets of replicate analyses. Values
are mean relative percent differences in sets of replicates with detected
values.
b Recovery determined by multiple analyses of matrix spike samples.
are mean relative percent recoveries.
Values
c Recovery determined by multiple analyses of standard reference material
(oyster tissue). Values are mean relative percent recoveries.
d Recovery determined by multiple analyses of standard reference material
(bovine livers). Values are mean relative percent recoveries.
e Because of the high recoveries of arsenic and lead relative to the certified
reference material, all data values for these substances in fish livers
were qualified as questionable.
2.43
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TABLE 2.3. SUMMARY OF AVAILABLE PRECISION AND RECOVERY DATA
FOR COMMENCEMENT BAY ORGANIC CHEMISTRY SAMPLES
Phenols
Aromatic hydrocarbons
Chlorinated hydrocarbons
Total PCBs
Phthalates
Miscellaneous compounds
Benzyl alcohol
Dibenzofuran
Surface
Sediments
Subsurface
Sediments
English Sole
Muscle
Livers
Precisions (Mean Coefficient of Variation)
± 52
± 17
± 25
±42
+ 61
±42
+ 18
± 41
± 15
+ 44
-
-
-
+_ 11 ^15
+ 100
+_ 54
+ 17
± 42
+ 9
+ 34
Phenols
Aromatic hydrocarbons
Chlorinated hydrocarbons
Phthalates
47 (59)
80 (99)
31 (120)
71
Percent Recoveryb
69 (67) 17 (67)
60 (94) 33 (98)
17 (140) 11 (124)
59 44
a Precision determined by multiple sets of replicate analyses. Value shown
is mean coefficient of variation in sets of replicates with detected values
(recovery corrected).
b Values shown are mean percent recoveries of isotopically labeled compounds
added in quantities within a factor of ten of the lower limit of detection. The
values in parentheses are the mean percent recoveries obtained from multiple
matrix spike samples. The matrix spike compounds were added at levels several
times higher than the isotope recovery standards.
2.42
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• An assessment of exposure to one or more substances
• An assessment of the hazard associated with exposure to
a substance or collection of substances.
These two elements must then be integrated into an analysis of the level
of risk experienced by a group, or population. This integration can be
accomplished on different levels: the risk to each exposed individual
over a lifetime can be calculated, or the cumulative risk to the entire
exposure population can be predicted as the total number of illnesses expected
over a 70-yr period.
Each major step in the risk assessment process (i.e., exposure evaluation,
hazard evaluation, and risk calculation) is discussed individually in the
following sections.
2.11.1 Exposure Evaluation
This analysis addresses three types of exposure: ingestion of fish
muscle tissue, ingestion of crab muscle tissue, and ingestion of fish livers.
Ingestion of fish and crab muscle tissues are analyzed differently from
ingestion of fish livers.
2.11.1.1 Exposure to Contaminants in Fish and Crab Muscle Tissue--
There are two elements to assessing exposure to the population eating
fish and crabs from Commencement Bay: 1) estimating the exposure population
and 2) estimating the rate of fish and crab ingestion. Estimates of these
elements rely on data from the Tacoma-Pierce County Health Department (TPCHD).
The TPCHD conducted a survey of recreational anglers in 1981, questioning
survey participants on the amount and type of fish they catch, the frequency
of their fishing, and their plans for the catch (whether they planned to
eat it). This catch/consumption survey was conducted during the late summer
and fall of that year, and focused on shore fishing activities.
The catch/consumption survey is detailed in a report by Pierce et
al. (1981). The authors (Pierce et al. 1981) concluded that 2,900 persons
fished the shores of Commencement Bay, with varying frequency, in that
year.- The estimate did not include results of the abbreviated survey of
persons fishing from boats. For this analysis, results from that part
of the survey have been adjusted for seasonal frequency following the method
of Pierce et al. (1981) for shore fishing. The frequency of boat fishing
was assumed to be equal to the frequency of shore fishing. The number
of persons fishing from boats (an estimated 1,170) was added to the number
fishing from shore to derive a total of 4,070 anglers. It was assumed
that the shore fishing and boat fishing populations did not overlap and
that persons fishing were not "double counted." It is quite likely, however,
that the addition of boat anglers resulted in an overestimate of total
exposed population. Pierce et al. (1981) reported that the average family
size is 3.74 persons. Assuming that all members of a family eat fish,
the total exposed population would be 4,070 x 3.74, or approximately 15,200
persons.
2.44
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Data from Pierce et al. (1981) also enable estimation of the frequency
of fishing, which (when combined with a value from the survey on average
catch per fishing trip) can be keyed to the amount of fish and crabs eaten.
A frequency distribution of fish muscle tissue ingestion rates from this
survey is presented in Table 2.5. The maximum ingestion rates reported
by Pierce et al. (1981) are used throughout this report as a basis for
estimating contaminant exposure. The risk assessment is keyed to this
table, because the risk to persons eating Commencement Bay fish and crabs
daily is considerably different from the risk to persons fishing only once
or twice a year and eating those fish. No data on shellfish (i.e., crab)
consumption were available for Commencement Bay. Consumption of crab was
therefore assumed to follow a distribution equal to fish consumption.
Rates of fish and crab ingestion (g/day) were multiplied by the average
level of contaminant (ug/g of fish) to yield exposure (ug/day). Exposure
calculations in this assessment were based on a number of scenarios. The
average level of contaminant in fish was calculated for:
• Each station from which fish or crabs were collected for
analysis
• Each waterway or study area (all stations within that area
combined)
• All nearshore/tideflats stations together.
In all cases, the method detection limit was used in the calculation of
means if a substance was not detected.
For this analysis it was assumed that the fish and crabs examined
for contaminants were representative of those ingested by persons fishing
in Commencement Bay. However, all fish analyzed were English sole, which
are not conmonly eaten and are among the most contaminated fish species
in Commencement Bay (see Section 3.6, Bioaccumulation). All shellfish
analyzed were Dungeness crabs and rock crabs. Data were not sufficient
to state that crabs were either more or less contaminated than other types
of shellfish in the Bay.
2.11.1.2 Exposure from Ingestion of Fish Livers--
A subgroup of special interest in this assessment was the population
that eats fish livers. Although this group is believed to be small, its
exposure to contaminants in Commencement Bay fish may exceed that of the
group eating muscle tissue because many chemicals are known to concentrate
in the liver.
The assessment of exposure from eating livers was based on the maximum
observed chemical concentrations in composite samples of livers from fish
captured at the trawl transects in the bioaccumulation study (see Section
3.6). Means were not used because several livers were pooled for each
chemical analysis, and the maximum observed values actually represent the
mean of several liver samples.
2.45
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TABLE 2.5. POPULATION EXPOSED BY CONSUMPTION RATE
Frequency
Daily
Weekly
Monthly
Bimonthly
Semiannually
Annual
Total
Frequency
Percent
0.2
6.6
11.4
7.3
17.2
57.3
100.0
Ingestion
Rate
1 Ib/day
1 Ib/wk
1 Ib/mo
1 lb/2 mo
1 lb/6 mo
1 Ib/yr
Intake
g/day
453.0
64.7
15.1
7.4
2.5
1.2
Population
Exposed
30
1,005
1,735
1,111
2,618
8,721
15,220
Reference: Pierce et al. (1981).
2.46
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No data on the quantity of fish liver eaten were available. It was
therefore assumed that the amount of liver eaten is proportional to the
amount of fish muscle eaten (i.e., that persons who eat fish livers consume
the livers from all fish they catch and consume). The average proportion
of liver weight to muscle weight for 13 species of Commencement Bay fish
is 0.12 (Gahler et al. 1982), the factor used in this analysis in scaling
exposures. Data on liver consumption rates as a function of muscle tissue
consumption rates are presented in Table 2.6.
2.11.2 Health Effects (Hazard Assessment) Methodology
Carcinogenic and noncarcinogenic health effects of U.S. EPA priority
pollutants are summarized in Table 2.7. These effects are associated with
different types of data and are treated differently in the risk assessment
process. Although some chemicals have multiple effects, only the most
significant (in severity or in terms of occurring at the lowest dose) are
discussed.
"Carcinogens" in this assessment are substances that the U.S. EPA
considers possible cancer-causing agents; they have not been implicated
as causes of cancer in humans in all cases. Most of the available data
are derived from animal studies, for both evidence and strength of carcino-
genicity. It is generally assumed that carcinogens do not exhibit threshold
effects (i.e., any exposure, no matter how low, can be associated with
a quantifiable cancer risk). The potency of the carcinogen is expressed
as a risk score, which is the probability of effect per unit dose of chemical,
in units of (mg/kg/day) ~1. The unit cancer risk scores in this study are
those published by the U.S. EPA's Carcinogen Assessment Group (U.S. EPA
1984).
Noncarcinogens are usually assumed to exhibit thresholds (i.e., to
cause some ill effect only after a certain dose is exceeded). That dose
is termed the No Observed Effect Level (NOEL). Since NOELs have been derived
almost exclusively from studies of small mammals, the measured NOEL is
usually divided by a safety factor to derive a level that can be considered
safe for humans. The safety factor takes into account the variability
in toxicity of a chemical between the experimental species and humans,
variability within the human population, and deficiencies in the experimental
data. The safety factor usually reflects a chronic, 70-yr exposure. This
resulting value is termed the Acceptable Daily Intake (ADI) and was used
in this assessment. Effects are considered possible in a sensitive subpopula-
tion when the exposure or dose exceeds the ADI (i.e., if the ratio of exposure
to the ADI equals or exceeds 1). ADIs are set for chronic (i.e., 70-yr)
exposure. Safety factors range from 1 [for high-quality data, based on
long-term human exposure (usually occupational)] to 1,000 (if the original
health data are from short-term studies of small lab animals).
2.11.3 Risk As sessmen t Ca1cu1 at ions
The exposure and effects data discussed above were combined in this
step of the assessment to calculate risk to the individuals ingesting fish
from Commencement Bay. Risk was assessed on a chemical-by-cherrncal basis.
Chemicals may interact with one another to produce synergistic effects
(magnifying the probability or severity of an effect), additive effects
2.47
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TABLE 2.6. FISH LIVER CONSUMPTION RATES
Frequency
Daily
Weekly
Monthly
Bimonthly
Twice/year
Yearly
Fish Consumption
g/day
453.0
64.7
15.1
7.4
2.5
1.2
Liver Consumption
g/day
54.4
7.8
1.8
0.9
0.3
0.1
Reference: Derived from Pierce et al. (1981) and Gahler
et al. (1982).
2.48
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TABLE 2.7. A SUMMARY OF HEALTH EFFECTS DATA
FOR CARCINOGENS AND NONCARCINOGENS
CHEMICAL
CARCINOGENS
acrylonitrile
aide in
arsenic
benzene
benzidine
beryllium
carbon tetrachloride
chlordane
chromium
hexachlorobenzene
dichloroethane (1,2)
trichloroethane (1,1,2)
tr ichloroethane (1,1,1)
tetrachloroethene
tr ichloroethene
tetrachloroethane (1,1,2,2)
hexachloroethane
trichlorophenol (2,4,6)
chloroform
DDT
dichloroethylene (1,1 and 1,2)
dieldrin
dinitrotoluene
tetrachlorodioxin
diphenylhydrazine
halomethanes
heptachlor
heptachlor epoxide
hexachlorobutadiene
hexachlorocyclohexane (HCH)
alpha
beta
gamma (Lindane)
dimethyl nitrosamine
diethyl nitrosamine
dibutyl nitrosamine
NN diphenylamine nitrosamine
N-nitrosodipropylamine
dibenzo (a , i ) pyrerve
benzo(a)pyrene
DEI IP
PCBs
toxaphene
tetrachloroethylene
trichloroethylene
vinyl chloride
BCEE
RISK SCORE
per mgAg/day
0.552
11.4
14
0.052
234
4.86
0.083
1.61
41
1.67
0.037
0.0573
0.0016
0.035
0.019
0.201
0.0142
0.0199
0.183
8.42
1.04
30.4
0.311
425000
0.768
0.183
3.37
3.76
0.0775
4.75
11.1
1.84
1.33
25.9
43.5
5.43
0.0049
31
476
11.5
0.0141
4.34
1.13
0.04
0.0126
0.0175
28
HEALTH
EFFECT
brain timers
liver tumors
skin cancer
leukemia
bladder cancer
leukemia
liver tunors
liver cancer
when inhaled; no value for ingested
liver tumors
circulatory henangiosar comas
hepatocellular carcinomas
liver tumors
liver tumors
liver tumors
hepatocellular carcinomas
hepatocellular carcinomas
hepatocellular carcinomas, adenomas
hepatocellular carcinomas
liver adenocarcinoma
kidney adenocarcinoma
liver tumors
mammary tumors, hepatocellular carcinoma
hepatocellular and other carcinomas
hepatocellular carcinomas and adenomas
liver tumors
hepatocellular carcinoma
hepatocellular carcinoma
renal tubular adenoma and carcinoma
liver tumors
liver tumors
liver tumors
liver tumors
liver cancer
liver cancer
bladder and esophogeal cancer
bladder tumors
mammary tunors and hepatocarcinoma in mice
lutvj cancer- inhalation
stomach papillomas, carcinomas
liver, kidney cancsr
hepatocellular carcinoma
hepatocellular carcinoma and adenoma
hepatocellular carcinoma
hepatocellular carcinoma
liver angiosarcoma
various carcinomas
2.49
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TABLE 2.7. (Continued)
CHEMICAL
NONCARCINOGENS
ADI
ug/day
SAFETY HEALTH
FACTOR EFFECT
acrolein
ODD
DDE
a-endosulfan
b-endosulfan
endosulfan sulfate
endtin
endrin aldehyde
antimony
cadmium
chromium-VI
chromium-Ill
cyanide
lead
mercury
manganese
nickel
selenium
silver
thallium
zinc
fluorotrichloromethane
dichloroethane (1,1)
dichloropropane (1,2)
dichloropropane (1,3)
dichloropropylene (1,3)
hexach1orocyc1opentadiene
bis 2-chloroisopropyl ether
chlorobenzene
dichlorobenzene (1,2)
dichlorobenzene (1,3)
dichlorot>enzene (1,4)
trichlorobenzene (1,2,4)
ethylbenzene
nitrobenzene
toluene
total xylenes
phenol
chlorophenol
dichlorophenols
pentachlorophenol
nitrophenols
dinitrophenol
dimethylphenol
dinitro-o-cresol
diethylphthalate
dimethylphthalate
di-n-butylphthalate
di-n-octylphthalate
acenaphthene
fluoranthene
naphthalene
1100 1000 unknown via oral exposure
3010 1 hunched appearance, increades urination
350 1 hepatic necrosis in rats
280 100 brain and kidney damage
280 100 brain and kidney damage
280 100 brain and kidney damage
70 100 nervous system, leukocytosis, kidney degeneration
70 100 nervous system, leukocytosis, kidney degeneration
292 100 altered blood chemistry
700 ? renal tubular necrosis in humans
175 1 kidney tubular necrosis
357000 1 sterility
330 100 hypoxia (oxygen blockage)
100 ? brain dysfunction and anemia in humans
20 10 ataxia,cerebellar atrophy, impaired vision in humans
10000 ? neurological dysfunction in humans
1460 1000 fetal mortality or reduced body weight
700 10 liver and endrocrine gland effects
16 5 kidney hemorrhage, liver, stomach, and intestine damage
37 1000 nerve, kidney, liver, and stomach damage
15000 100 copper deficiency and anemia in humans
201000 10 cardiac arrythmia
8100 ? liver function changes
980 1 liver function changes
180 1000 liver function changes
180 1000 liver function changes
36 100 no oral effects known
70 10 no oral effects known
1008 1000 nervous systen depression; liver, kidney necrosis
107000 100 cirrhosis of liver
140000 100 cirrhosis of liver
161000 100 cirrhosis of liver
464 10 liver metalwli.sm changes in monkeys
1600 1 weight increase, kidney effects
4000 10 blood cyanosis in humans by inhalation or dermal exposure
134000 100 nervous system effects and cardiac arrythmia
160000 10 maternal toxicity
6800 500 kidney and liver damage
6900 1000 increased nervous response in humans
7000 10.00 convulsions in cats
2100 100 micro-level changes in human liver and kidney via inhalation
140 1000 effects unknown
140 1 numerous for 2,4- eyes, skin, nerves, liver, spleen in humans
7000 190 liver, spleen pathology
71 10 effects on human skin when inhaled
875000 100 decreased growth
1800 10 kidney effects on humans when inhaled
1800 10 brain abnormalities in humans when inhaled
1800 10 effects unknown
18 ? enzyme blood changes in humans when inhaled
420 1 mortality at high dose via dermal contact
18000 10 cataracts in humans (inhalation), rats (oral)
Reference: U.S. Environmental Protection Agency (1983, 1984)
2.50
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(combining similar effects of two chemicals), or antagonistic effects (pre-
venting an effect entirely or lessening its severity). However, evidence
of these interactions is relatively weak. Furthermore, while the combined
effect of two chemicals may be known, the combined effect of the complex
mixture of Commencement Bay pollutants is unknown.
2.11.3.1 Calculation of Carcinogenic Risk--
The first step in the assessment of carcinogenic risk was to calculate
the exposure of an individual to a contaminant. Exposure was calculated
as:
E = CI/W
where:
E = Exposure, mg/kg/day
C = Contaminant concentration, mg/kg
I = Ingestion rate, kg/day
W = Human weight, kg (assumed 70 kg).
The exposure was then used to calculate individual risk as:
Ri = BE
where:
RI = Individual lifetime risk
B = Risk score, (mg/kg/day)"1.
Individual risk can be multiplied by the number of persons exposed
at that level to estimate the total number of persons expected to develop
cancer among the exposed population over the 70-yr lifetime. That calculation
was not performed for all chemicals in this risk assessment. It was performed
only for the chemicals with the highest absolute risks because other chemicals
resulted in very low risks that were well below the health risk criterion
(i.e., one predicted cancer case in the exposed population).
2.11.3.2 Noncarcinogenic Risk Calculations--
Because noncarcinogenic chemicals exert a threshold effect, the assessment
of risk at a calculated level of exposure was performed by comparing the
exposure to the ADI. If exposure exceeded the ADI, all persons exposed
at that level were assumed to be affected. If exposure was equal to or
less than the ADI, none of the individuals were assumed to be affected.
There is no provision in this method for degree of effect. However, to
a limited degree, the ratio of exposure to the ADI indicates the weight
of evidence of projected effects.
2.51
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2.12 SOURCE IDENTIFICATION
2.12.1 Sediment Chemistry
2.12.1.1 Surficial Sediment Chemistry--
All source identification efforts were initiated by an assessment
of the magnitude and spatial extent of contamination in the surficial sediments
of defined problem areas. The spatial gradient of contamination was evaluated
to determine the probable location of the contaminant sources. The implicit
assumption in this evaluation was that sediments with the highest levels
of contamination (with appropriate normalization, as discussed below) were
closest to the contaminant sources. It is recognized that in certain high-
energy environments, physical transport processes may alter the contaminant
distribution so that the greatest level of contamination does not necessarily
coincide with the location of the contaminant source. Within the waterways
of Commencement Bay, tidal action provides the only effective mechanism
of contaminant dispersal. Therefore, it is reasonable to assume that environ-
mental release of a contaminant would be reflected in nearby sediments,
particularly if that contaminant has a high affinity for adsorption to
sediment particles or organic matter, as do many of the contaminants of
concern.
The spatial gradient of contamination was used both to determine the
location of contaminant sources and to suggest probable routes of contami-
nation. The guidelines used in this assessment are shown below. Final
determinations of probable sources and routes of contamination required
the integration of a great diversity of data and final assessments were
made on a case-by-case basis. General guidelines for source identification
efforts included:
• A localized area of contamination close to a known industrial
outfall, storm sewer, or other discharge implicated that
discharge as a potential source.
• A localized contaminant "hot spot" far from any identified
potential source suggested the occurrence of a spill or
exposed sediments from an unidentified historical source.
• A localized area of contamination in the general vicinity
of a potential source but not immediately adjacent to an
outfall suggested groundwater as one of the potential sources.
Historical waste disposal practices on nearby properties
were examined. A spill or historical source represented
other possible explanations.
t Contaminant concentrations that decreased from the mouth
of the waterway to the head suggested either the presence
of a source very near the mouth or advection of the contaminant
into the waterway from other areas.
Sediment contaminant concentrations are typically expressed as the
weight of the contaminant per dry weight of sediment (hereafter referred
to as "dry-weight basis"). In some cases, it was also valuable to normalize
2.52
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the concentrations using some other sample variable (see Section 3.1.2).
For example, metals concentrations are sometimes shown on a dry-weight
basis and normalized to percent fine-grained sediment (silt and clay),
since metals generally have a high affinity for the finer silt and clay
particles. This normalization is reported in the present study of sources
only when the normalized data show a trend not apparent in the distribution
of dry-weight concentrations. Organic compound concentrations are typically
shown on a dry-weight basis and normalized to the total organic carbon
content of the sediments, since the organic compounds of concern generally
have a high affinity for organic material. Normalization of organic compounds
by sediment organic carbon content can help reduce the effects of variable
sediment texture on the interpretation of contaminant spatial trends.
These data are also useful in evaluating the influence of organic enrichment
on contaminant accumulations.
Normalizations of sediment chemistry data to account for variations
in grain size or organic carbon content are used in interpretations only
when they provide additional information not apparent in the spatial pattern
of dry-weight concentrations. Large amounts of wood chips or slag in the
sediments could also reduce the usefulness of these normalizations.
Throughout the source evaluation section (Section 7), two formats
are used for presentation of surficial sediment chemistry data: 1) a graph
of contaminant concentration versus distance from waterway mouth, and 2)
a plan view of the relevant study area showing location of the sampling
stations and the contaminant concentrations at each station (Figure 2.8).
The concentration versus distance graphs were used only for long, linear
waterways (Hylebos and City) when contaminant gradients along the length
of the waterway were of primary interest. Plan views were used for all
areas of concern, and were particularly valuable in identifying cross-waterway
gradients of contamination. In some cases, plan views were used during
data analysis and only critical features are summarized in text.
Three data types are differentiated on the graphs of concentration
versus distance: 1) quantified contaminant concentrations; 2) "less than"
values when a single compound was above a detection limit and below a quantifi-
cation limit or when one member of a compound group was unquantified; and
3) undetected values, in which case the detection limit is shown. Source
of the data is further differentiated on the graphs. In a few cases, data
are not shown on the figures because they were from laboratory analyses
with disproportionately high detection limits. Criteria for exclusion
are provided below:
• For individual substances (or traditionally defined mixtures
such as PCB Aroclors), undetected values at a detection
limit greater than 100 ppb that also exceeded the 80th percentile
of detected values were eliminated from the graphs.
t For groups of substances, data values for group totals were
excluded from graphs if:
The average detection limit of the individual undetected
components exceeded 100 ppb, and
2.53
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o<
*5
.0
O,
a
n
v
I
u
o
u
700
600 -
500 -
400-
300 -
200 -
100 -
O Tetri Tech Investigation - quantltated value
0 Other Investigations - quantltated value
A Tetra Tech Investigation - less than value*
V Other Investigations - less than value*
+ Tetra Tech Investigation • undetected value
X Other Investigations - undetected value
a
o
o
o
0 0
(A)
246
(Thousonds)
Ft. from mouth of waterway
•For single compounds a less than value Indicates the compound was present at a concentration
above the detection limit but below the quantHatlon Halt. For conpound groups* a less than
value Indicates one or nore members of the group was below the detection or quantltatlon Unit.
O Tetra Tech Investigation
* UOOE. 1984 data (not shown)
0 UOOE, historical data (not shown)
A EPA data
X Data fro* other agencies
(B)
Figure 2.8. Examples of surficial sediment chemistry data.
2.54
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The sum of the detection limits for undetected components
in the group was greater than 50 percent of the total
value for the group, and
The group sum also exceeded the 80th percentile of
group sums where all components were detected or where
undetected components constituted less than 50 percent
of the total.
Plan views of the study area showing station locations and contaminant
concentration at each station (Figure 2.8) were shown when cross-waterway
gradients provided the most information about source location. Data shown
on these figures were subject to the same review process described above.
"Less than" or undetected values were indicated by "L" or "U," respectively.
Station locations are shown by symbols indicating the agency responsible
for collecting the data.
2.12.1.2 Sediment Cores--
Box core and gravity core samples were taken to obtain information
on the vertical distribution of contaminants within the sediments (see
Section 2.2.1) and on temporal changes in contaminant input to the waterways.
Several guidelines were used in this assessment:
• Greatest contaminant concentrations in the uppermost horizon
suggested an ongoing or a recent contaminant input.
• Subsurface contaminant maxima suggested that the greatest
contaminant inputs had occurred historically or that the
area had recently been covered by clean material (e.g.,
by dredging activity).
• Elevated contaminant concentrations within a single discrete
horizon suggested that a spill, or a discharge of short
duration was responsible.
§ Uniformly elevated contaminant concentrations throughout
the sediment column suggested either long-term contaminant
input, contamination via groundwater percolating up through
the sediments, or mobility of the compound in interstitial
water.
For closely spaced core samples (e.g., in lower Hylebos Waterway), data
from only one representative core sample are illustrated and the comparability
of the other cores is discussed. All available core data were considered.
Sediment core data are usually presented in tabular form in Section 7.
Data from several compounds in multiple cores are presented as illustrated
as in Figure 2.9. A logarithmic scale was used because contaminant concen-
trations with depth typically varied over an order of magnitude or more.
Although concentrations on both a dry-weight and normalized basis were
considered, only concentrations on a dry-weight basis are shown to simplify
the graph. Only one contaminant concentration per horizon is shown, since
sediments from throughout the horizon were homogenized before analysis.
2.55
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TJ
O>
1,000
Concentration (yg/kg)
10,000
100,000
0.2-
0.4-
o.
O)
o
jLJL
Low molecular weight PAH
High molecular weight PAH
Figure 2.9. Example of sediment core data illustrating con-
centrations of PAH with depth in sediment at a
site within Hylebos Waterway.
2.56
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It should be recognized that contaminant concentrations could vary within
any given depth interval.
2.12.2 Water Quality Data
Contaminant concentration of suspended particulates were determined
for samples collected during water quality surveys of April and August,
1984. For organic compounds, the utility of these data in source identifi-
cations was limited because concentrations were usually below detection
limits (except for some PAH). Metals concentrations were typically above
detection limits. For contaminants with quantifiable concentrations, these
data were used as ancillary information in source identification efforts.
The data were used to estimate the importance of contaminant advection
between Commencement Bay and the individual waterways.
2.12.3 Point Sources and Runoff
The contribution of contaminants by point sources and runoff was assessed
by use of loading estimates. These loading estimates were calculated from
all available measurements of discharge flow rate and contaminant concentration
in the Comnencement Bay database. The majority of discharge flow and concen-
tration measurements in the database have come from WDOE investigations
(e.g., Class II surveys) and Commencement Bay Nearshore/Tideflats Remedial
Investigation studies. Other discharge-related data were available from
surveys conducted by U.S. EPA, Tacoma-Pierce County Health Department,
and specific industries. A thorough discussion of the discharge-related
data in the Commencement Bay database is provided in Tetra Tech (1984b) .
Data appear in Appendix XV.
For each contaminant of concern, an average loading was calculated
for each discharge into the defined problem area for which flow and concen-
tration data were available. Because of the diversity of discharge data
sources and the variability in data gathering and reporting methods, guidelines
were established to ensure consistency in calculating average contaminant
loadings. Procedures were established to deal with: 1) unmeasured flow
rates; 2) undetected values; 3) detected but unquantitated concentrations
("less than" values) for single compounds; 4) loading estimates for a contami-
nant group when one or more members of the group were undetected; 5) loading
estimates for a contaminant group when one or more members of the group
were unquantitated; and 6) loading estimates for a contaminant group when
one or more members of the group were unmeasured. These procedures are
discussed below and are illustrated in Figure 2.10.
• Unmeasured Flow Rates: An average contaminant loading for
a discharge was determined by calculating an average of
all available flow measurements and an average of all concen-
tration measurements for the contaminant of concern. The
average flow and average concentration were then multiplied
together, with appropriate adjustments for units, to obtain
an average loading. This procedure allowed maximum use
of all available data. In particular, it permitted the
use of concentrations for which there was no coincident
flow measurement.
2.57
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I. UNMEASURED FLOW RATES
Contaminant
Sampling Flow Concentration
Event (MSP) (uq/1)
1 0.5 9
2 1.5 S
3 not icasured ZS
I • 1.0 1-13
Avg loading • 1.0 x 13 x 0.00834 - 0.11 Ibs/day
0.00634 • conversion factor for Blcrograms to povmds and gallons to liters
2. UNDETECTED VALUES
1 0.5 2
2 1.5 undetected at 30
3 1.0 5
7-1.0 I . 3.5
Avg loading • 0.029 Ibs/day
3. DETECTED Biff UHQUAKTITATED CONCENTRATIONS ("LESS THAN* VALUES) FOR SINGLE COMPOUNDS
1 0.5 2
2 1.5 10
3 _ *-° <9
7-1.0 7-<7
Avg loading • <0.058 Ibs/day
<• IOAPIH6 ESTIMATES FOR A COHTAH1NANT 6ROUP WHEN ONE OR MORE MEMBERS OF THE 6ROUP HERE UNDETECTED
Sailing Flow Concentration hiq/1)
Event (H60)
1 0.5
2 1.5
3 1.0
7 - 1.0 7-20
Avg loading • 0.17 Ibs/day
5. LOADING ESTIMATES FOR A COKTAHINANT GROUP WHEN ONE OR MORE MEMBERS OF THE 6ROUP MERE UNQUAHTITATED
1 0.5 10 10 20
2 1.5 25 5 30
3 1.0 10 <15 <25
7-1.0 I . <25
Avg loading » 0.21 Ibs/day
6. LOADING ESTIMATES FOR A COHTAH1NAKT 6ROUP WHEN ONE OR MORE MEMBERS OF THE GROUP MERE PLEASURED
1 0.5 10 10 20
2 1.5 11 not Measured 11
3 1.0 15 5 20
7-1.0 Tt . 17
Avg loading • 0.14 Ibs/day
Naphthalene
10
25
10
Phenanthrene
10
5
undet. at 30
Total1
20
30
10
•Concentrations of «any compounds were sunned to obtain the total polycycllc aromatic hydrocarbon (PAH)
concentration though only two art shown here to simplify the presentation.
Figure 2.10. Examples of procedures used in calculating
average discharge loads.
2.58
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• Undetected Values: Undetected values were not used in calcu-
lating average concentrations and loadings. It was necessary
to exclude these observations because of the extreme variation
in detection limits among the surveys included in the Commence-
ment Bay database. The example in Figure 2.10 (Case 2)
is typical of the range of detection limits found in the
database. Chemical analyses of a particular discharge that
were characterized by high detection limits are so noted
in Section 7 (Source Evaluation), since the discharge could
be a significant but unquantified contaminant source.
• Detected but Unquantitated Concentrations for Single Compounds:
If a contaminant concentration exceeded a detection limit
but was less than a quantitation limit, it was reported
in the database as less than the quantitation limit. Such
values were included when calculating an average concentration
or loading since it is reasonable to assume that the actual
concentration may be at least half the quantitation limit.
• Loading Estimates for a Contaminant Group When One or More
Members of the Group Were Undetected: See Undetected Values,
above. The total group concentration does not include undetected
values, but only measured concentrations or "less than"
values.
• Loading Estimates for a Contaminant Group When One or More
Members of the Group Were Unquantitated: When the concentration
of one or more members of a contaminant group were detected
but Unquantitated ("less than" value), the quantitation
limits of those members were included in the total group
concentration. The group concentration was then reported
as less than a specified value.
t Loading Estimates for Contaminant Group When One or More
Members of the Group Were Unmeasured: When the concentration
of a contaminant group in a discharge was determined (e.g.,
total chlorinated butadienes, total PAH), the individual
compounds included in the group sum may have varied from
survey to survey. Analyses in which more compounds of the
group were measured will yield higher loading estimates
than analyses in which fewer compounds were measured. In
practice, however, the actual bias was minimal. Since regulatory
agencies typically test for an established suite of compounds
(i.e., priority pollutants), there were relatively few instances
in the database when all surveys did not consistently measure
the same suite of contaminants within a group. For the
few instances when such inconsistencies did occur, effects
on the calculated loading were noted in the test.
Source loading data for Commencement Bay are of limited and uneven
quality. This factor often constrained the conclusions concerning potential
sources.
2.59
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2.12.3.2 Average Mass Flux Estimates--
After initial identification of probable sources of a contaminant,
a review was performed to determine if the suspected contaminant inputs
adequately accounted for the observed levels of contamination. This determi-
nation was made using a mass flux approach as a first approximation only.
These calculations are not used to develop a mass balance for contaminants
in Commencement Bay. Limitations to the use of this approach in data interpreta-
tion are summarized below after the following discussion of conceptual
terms.
If the mass of sediment deposited over a given waterway within a given
time period can be established, then the mass of contaminant deposited
within this area can also be estimated. The time frame to achieve a given
average contaminant concentration can also be estimated. The concentra-
tion of a contaminant in surficial sediments can be expressed as:
Contaminant Concentration = Contaminant flux to the sediment surface
Sediment flux to the sediment surface
Rearranging the expression and including appropriate units yields:
Contaminant Flux (mg-cm'2-yr'1) = Concentration fmg/kq) x
Sediment Flux (mg-cm'2-yr'l) x 10'6 kg/mg
Sediment flux was the most difficult to quantify but was estimated from
the work of Carpenter et al. (1985) in which flux was estimated for 44
core samples taken throughout Puget Sound. Values ranged from 46 to 1,200
mg«cm~2-yr~l with an average of 336 mg-cm'^-yr"1. Sediment accumulation
rates in Commencement Bay waterways can be higher than those in the main
body of Puget Sound, because of higher inputs of terrestrial-derived particu-
lates. Despite this limitation, the maximum sediment flux observed in
the sound by Carpenter et al. (1985) (1,200 mg-cm'2-yr-l) was used to provide
an order-of-magnitude estimate of actual sediment flux in the waterways.
Substituting 1,200 mg.cm-2-yr-l in the equation above yields:
Contaminant Flux (mg.cm~2.yr-l) = Concentration (mg/kg) x 0.0012 kg.an-2.yr-l
This average contaminant flux is the mass of contaminant that would
have to be introduced to the waterway to achieve the observed average level
of sediment contamination, assuming no advection into or out of the system.
It is referred to hereafter as the concentration-derived mass flux. No
assumptions were made regarding the actual distribution of the deposited
material in the waterway; the calculations reflect the overall average
estimated flux only.
An average contaminant flux based on known loadings of the contaminant,
referred to hereafter as the source-derived mass flux, can be estimated
if the surface area over which the contaminant is deposited is known:
Contaminant Flux (mg-c.n-2.yr-l) = Loading (Ib/day) x 1.65x108
v y ' Surface area of deposition (cm2)
where 1.65 x 10& is a coefficient to convert Ib to mg and days to years.
2.60
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If it is assumed that the contaminant is deposited in sediments
throughout the waterway, the waterway surface area can be used in the ex-
pression. The surface areas used in these calculations were: Hylebos
Waterway, l.OxlO10 cm2; Sitcum Waterway, 1.6xl09 cm2; St. Paul Waterway,
l.SxlO9 cm2; Middle Waterway, 9.8xl08 crn^; and City Waterway, 4.5xl09 cm2.
No assumptions were made regarding the actual depositional pattern of the
contaminant within these areas.
The average contaminant concentration in the waterway was determined
and used to calculate a concentration-derived mass flux (i.e., the mass
of the contaminant that would have to be deposited in the waterway in a
given time period to attain the observed average concentration). The sum
of known source loadings for the contaminant was then determined and used
to calculate a source-derived mass flux (i.e., the mass of contaminant
estimated to be entering the waterway from identified sources).
Large uncertainties are associated with source loading data and estimated
sediment accumulation rates for the nearshore/tideflats area of Commencement
Bay. Therefore, the mass flux approach was used only to evaluate data
gaps in source loading information (i.e., whether major sources were unaccounted
for when the source-derived mass flux of contaminants was compared with
the average concentration-derived mass flux). The criteria used to determine
these potential data gaps were as follows:
• When the source-derived mass flux was at least two orders
of magnitude lower than (i.e., less than 1 percent of) the
sediment concentration-derived mass flux, the contaminant
was considered to have major unidentified sources. The
conclusion that major sources remained unidentified was
made on the basis of mass flux estimates only if this condition
was met. Even given the uncertainties of the analysis,
this conclusion is warranted because it identifies a potential
data gap.
• When the source-derived mass flux value was within two orders
of magnitude of the value for the sediment concentration-
derived mass flux, the two values were considered comparable
given the uncertainties of the analysis. No conclusions
concerning sources were made.
• When the source-derived mass flux value exceeded the sediment
concentration-derived mass flux by more than two orders
of magnitude, the two values were still considered comparable
within the uncertainty of the analysis. It might have been
inferred that the identified sources more than accounted
for the observed contamination, but sediment accumulation
rates might have been underestimated and source contributions
might have been overestimated. Hence, no conclusions concerning
sources were made.
Although the calculations and comparisons discussed in this section
were made for all available data, only the final results are summarized
in the source evaluation section of this report. If a contaminant was
2.61
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undetected in all available source data sets, no attempt was made to determine
mass flux estimates for that contaminant.
2.12.3.3 Reference Numbers--
All point source and runoff discharges to the study area for which
loading data exist, as well as some groundwater seeps, were identified
in Section 7 (Source Evaluation) by a five-character reference number (e.g.,
HK-052). These reference numbers were developed by the Tacoma-Pierce County
Health Department during drainage system investigations in which an attempt
was made to locate every seep, ditch, and drain within the nearshore/tideflats
area (Rogers et al . 1983). The reference system was expanded as part of
the present investigation to include additional discharges. Throughout
the text, each discharge is identified by its reference number and, if
available, a common name (e.g., HM-028 = Morningside Ditch) or descriptor
(e.g., HY-018 = 8-in steep pipe). A corresponding map of each waterway
is also provided.
2.12.4 Groundwater Sources
There is evidence of groundwater contamination within many portions
of the nearshore/tideflats area because of past spills, use of unlined
industrial waste ponds, and landfilling of hazardous materials. Dames
and Moore (1982) listed over 30 sites where past practices could be adversely
affecting groundwater quality. However, as noted by Tetra Tech (1984b),
adequate assessment of groundwater contamination is hampered by the absence
of reliable groundwater flow information throughout most of the tideflats.
Existing data are inadequate to determine the magnitude of groundwater
contamination, predict the route of groundwater flow from a contaminated
area, or determine the loading of contaminants to the waterways via groundwater.
Local, state, and federal agencies were contacted to obtain all available
well log data for information on groundwater flow, including the Port of
Tacoma, Tacoma Public Utilities Department, Pierce County Department of
Public Works, State Department of Highways, WDOE, and the U.S. Geological
Survey. From these inquiries, it became apparent that little well log
data exist for the tideflats west of the 1-5 corridor. The existing data
are spatially limited to selected properties investigated specifically
to assess the extent of groundwater contamination. These properties include:
• Occidental Chemical Corporation
• Three Occidental waste disposal sites (General Metals, Dauphin,
Petarcik)
• Pennwalt Corporation
• Kaiser Aluminum
• Allied Chemicals
• Georgia Pacific
§ D Street Petroleum Storage Area
2.62
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• Chemical Processors/Lilyblad Petroleum
• Tar Pits site
• Tacoma Spur
• Union Pacific Railroad yard
t Two U.S. Gypsum waste disposal sites.
These data were used in source identification when appropriate. For many
of these sites, the data were of limited utility because of inadequacies
in sampling and/or analytical methodology.
2.12.5 Atmospheric Sources
Available data from the Puget Sound Air Pollution Control Agency (PSAPCA)
and the U.S. EPA Air Work Group were examined to evaluate atmospheric source
emissions in the Tacoma area. Relevant information was scarce. PSAPCA
typically monitors total suspended particulate matter, sulfur oxides, nitrogen
oxides, volatile organic compounds, and carbon monoxide. Very little data
are available from either PSAPCA or U.S. EPA concerning the priority pollutants
and other contaminants identified to be of concern in the current investiga-
tions. Limited metals data were available from the high-volume filters
maintained around the Tacoma area by PSAPCA. These instruments are designed
to collect the small suspended particulates that would travel far from
the Tacoma area prior to deposition. Corresponding data do not reflect
the contaminant input potentially resulting from large particulates that
would be expected to enter the waterways directly from local industrial
fallout or through stormwater runoff (Nolan, J., personal communication).
2.12.6 Spills
Files of both the U.S. Coast Guard (USCG) and WDOE were reviewed to
obtain information on past spills of hazardous materials in the nearshore/
tideflats area. The USCG files were not useful in providing the type of
data required because of imprecision in reporting the spill location (i.e.,
to the nearest minute latitude and longitude). For example, a spill occurring
at 470 is1 N latitude and 1220 26' W longitude could have occurred in the
Puyallup River; St. Paul, Middle, or City Waterway; or the southeast portion
of Commencement Bay.
WDOE Environmental Complaint fields from 1979 to 1985 were also reviewed.
Within this 5-yr period, WDOE received reports of approximately 30 hazardous
material spills that could affect environmental quality in the waterways
or along the Ruston-Pt. Defiance Shoreline. Sulfuric acid spills (mostly
from ASARCO) constituted approximately one-third of this total. The remainder
included spills of plating wastes, paint, solvents, caustic, creosote,
fungicide, and sodium chlorate. In addition, about 35 petroleum spills
in excess of 50 gal occurred in the nearshore/tideflats during this same
period.
2.63
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Additional spill-related information was obtained from WDOE files
on specific industries. For areas of elevated sediment concentrations,
files were reviewed of all nearby industries that might handle products
containing the contaminant of concern. This file review uncovered many
additional spills not included in the Environmental Complaint files.
2.12.7 Dredging
The dredging history of the Nearshore/Tideflats area was reviewed
to help interpret horizontal and vertical contamination gradients observed
in the sediment core samples. Maintenance dredging activities were reviewed
and summarized in Dames and Moore (1981, 1982). Information on private
dredging activities within the nearshore/tideflats area was obtained by
a WDOE review of U.S. Army Corps of Engineers (COE) and U.S. EPA files.
All dredge and fill applications submitted to the COE from 1972 to the
present were reviewed to identify the industrial applicant, the spatial
extent of dredging activities, and the volume of material intended for
removal. Since COE records did not indicate whether the intended dredging
actually occurred or how much of the material permitted for removal was
actually removed, this information was obtained from U.S. EPA staff (Duane
Kama) or by phone calls to the applicants.
2.64
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3.0 RESULTS
3.1 SEDIMENT CHEMISTRY
The following sections provide a summary of chemical results for over
190 surface and subsurface samples of subtidal sediments collected from
Commencement Bay as part of the 1984 Superfund investigation. An additional
six sediment samples were collected from Carr Inlet reference stations
for complete chemical characterization. These data include blank-corrected
analyses for the 13 U.S. EPA priority pollutant metals, 3 additional metals
(including iron and manganese used as natural indicators), 78 extractable
U.S. EPA priority pollutant compounds, 12 additional U.S. EPA Hazardous
Substance List compounds, and selected tentatively identified compounds
for which all samples were analyzed. Twenty of the samples were also analyzed
for the 31 U.S. EPA volatile priority pollutants and/or 2,3,7,8-tetrachloro-
dibenzodioxin. The focus of these sections is to:
• Provide a chemical perspective of Commencment Bay study
areas, including the general distributions, concentration
ranges, and frequencies of detection of chemical contaminants
• Define groups of chemicals with similar spatial distributions
in Commencement Bay sediments and/or with similar chemical
characteristics
• Determine the magnitude of contamination relative to conditions
at Carr Inlet reference areas, and the significance of this
contamination relative to conditions at all Puget Sound
reference areas
• Condense the list of chemicals of concern to those detected
in Commencement Bay study area sediments at levels that
exceed Puget Sound reference area conditions
• Provide a summary list of Commencement Bay study areas,
segments within areas, and individual stations with the
highest levels of contamination for each chemical of concern.
3.1.1 Bulk Sediment Characteristics
Conventional analyses of bulk sediments included determination of
the grain size distribution, and concentrations of oil and grease, volatile
solids, total organic carbon, nitrogen, and sulfides. Results of these
analyses are summarized in Figures 3.1-3.5. Original data for individual
sediment samples are presented in Appendix III.
3.1
-------
PERCENT FINE-GRAINED SEDIMENTS (>4)*
UJ
S
0
LU
CO
g
UJ
u.
O
f-
01
o
cc
UJ
a.
100-1
80-
60 -1
40-
20-
1
r
i
I
L
>
<
T
1
_:'
JL
t
i
i
i
1
i
I
f
i
T
I ...
J
i
7-
1
I
i
1
J
I
r
i
i
i
T
*
JL
i
•
r
1.1
1 1
T -
HY BL
SI
Ml
SP MD Cl
RS
CR
RANGE
STANDARD DEVIATION
a SHADED AREAS INDICATE THE PERCENTAGE OF CLAYS (
DATA ARE FROM MARCH 1984 SEDIMENT ANALYSES ONLY (n=115)
b LOCATION OF PUYALLUP RIVER INDICATED BY ARROW.
STUDY AREAS SHOWN GEOGRAPHICALLY FROM NORTH (LEFT)
TO SOUTH (RIGHT).
Figure 3.1. Total average percent fine-grained material
(>4 phi) and average percent clay (>8 phi) in
sediments from Commencement Bay and Carr Inlet
study areas.
3.2
-------
OIL AND GREASE
4,300 - -
3000-1
2000-
g
LU
&
Q
o>
1000 H
if,
UPPER RANGE 5,700
4,100
RANGE
200-500
HY BL SI Ml
PU
MD Cl RS
CR
RANGE
STANDARD DEVIATION
aDATA ARE FROM MARCH 1984 SEDIMENT ANALYSES ONLY (n = 115)
b LOCATION OF PUYALLUP RIVER INDICATED BY ARROW.
STUDY AREAS SHOWN GEOGRAPHICALLY FROM NORTH (LEFT)
TO SOUTH (RIGHT).
Figure 3.2. Total average oil and grease concentrations in
sediments from Commencement Bay and Carr Inlet
study areas.
3.3
-------
O
COMMENCEMENT O
BAY
> 10% OC 5-10% OC < 5% OC
• CLOSED CIRCLES > 10ppm SULFIDES
O OPEN CIRCLES < 10ppm SULFIDES
METERS
1000
CITY
WATERWAY
Figure 3.3. Relative concentrations of sediment organic
carbon and sul fides in Commencement Bay study
areas (January and March, 1984).
-------
UJ
•
in
RUSTON
N
o
I
r
0
4000
I FEET
1 1 METERS
1000
TACOMA
O
COMMENCEMENT
BAY
> 10% OC 5-10% OC < 5% OC
• CLOSED CIRCLES > 10ppm SULFIDES
O OPEN CIRCLES < 10ppm SULFIDES
Figure 3.3. (Continued)
-------
RATIO OF
% TOTAL VOLATILE SOLIDS
TOTAL ORGANIC CARBON
6.0-1
5.0-
4.0-
O
O
3.0-
2.0-
1.0-
HY
BL
SI
Ml A. MD
PU
SP
Cl
RS
CR
I STANDARD DEVIATION
a LOCATION OF PUYALLUP RIVER INDICATED BY ARROW.
STUDY AREAS SHOWN GEOGRAPHICALLY FROM NORTH (LEFT)
TO SOUTH (RIGHT).
Figure 3.4. Comparison of the average percent total vola-
tile solids with average percent total organic
carbon in sediments from Commencement Bay and
Carr Inlet study areas.
3.6
-------
ATOMIC RATIO OF TOTAL ORGANIC CARBON
ATOMIC RATIO OF TOTAL ORGANIC N|TROGEN
60-1
50-
40-
O
30-
20-
10-
HY
f.
BL
SI
Ml ^ SP
pua
MD Cl
RS
CR
EXCLUDES AN ANOMALOUSLY HIGH C/N RATIO OF 210 AT MD-13;
THE AVERAGE INCLUDING THIS VALUE IS 87 ± 110.
I STANDARD DEVIATION
a LOCATION OF PUYALLUP RIVER INDICATED BY ARROW.
STUDY AREAS SHOWN GEOGRAPHICALLY FROM NORTH (LEFT)
TO SOUTH (RIGHT).
Figure 3.5. Comparison of the average atomic carbon/nitro-
gen ration (C/N) in sediments from Commencement
Bay and Carr Inlet study areas.
3.7
-------
3.1.1.1 Grain Size--
The average percent of fine-grained material (silt plus clay; >4 phi)
and the average percent of clay (>8 phi) in sediments of each study area
are displayed in Figure 3.1. The percent of fine-grained material (primarily
silt) tended to decrease north of the Puyallup River. This decrease probably
corresponds with a decrease in the load of silty material discharged by
the Puyallup River in a predominantly northward-trending plume. Major
discharges from stormwater drains at the head of City Waterway contributed
to the observed accumulation of fine-grained sediments in that waterway.
The range and variability in the percent of fine-grained sediments along
the Ruston-Pt. Defiance Shoreline were similar to those of reference sediments
from Carr Inlet. Sediments collected within Carr Inlet were substantially
coarser than most sediments sampled in Commencement Bay. Effects of this
difference in grain size on interpretations of chemical and biological
data are discussed in later sections.
3.1.1.2 Oil and Grease--
Average oil and grease concentrations (mg/kg dry sediment) for Commencement
Bay study areas are presented in Figure 3.2. Highest concentrations were
found in sediments from City Waterway and along the Ruston-Pt. Defiance
Shoreline. Oil and grease concentrations decreased from the head of City
Waterway to the mouth, suggesting a substantial contribution from drains
at the head of the waterway. Changes in the spatial distribution of oil
and grease concentrations along the Ruston-Pt. Defiance Shoreline suggest
multiple local sources. The highest dry-weight (DW) values were found
at Station RS-18 (4,100 mg/kg) off the main ASARCO plant outfall and at
Station RS-16 (2,100 mg/kg) along the shoreline (see Figures 2.1-2.3 for
station locations). Average oil and grease sediment concentrations in
other study areas were comparable to those measured at Carr Inlet.
3.1.1.3 Total Organic Carbon and Sulfides--
The extent of organic enrichment in Commencement Bay surface sediments,
as indicated by the percent total organic carbon (TOC) content, is summarized
in Figure 3.3. Measured TOC sediment values ranged from <1 percent at
several stations to 20.5 percent at Station RS-16 along the Ruston-Pt. Defiance
Shoreline. Sediments in the isolated Wheeler-Osgood branch of City Waterway
were also highly enriched (18 percent TOC). TOC levels in the remainder
of City Waterway sediments consistently declined from 8.9 percent at the
head of the waterway to 1.2 percent at the mouth. Other study areas having
major variations in TOC content included St. Paul Waterway (TOC range 1.5-16
percent), and Hylebos Waterway (TOC range 0.26-12 percent).
Sediment sulfide concentrations are summarized in Figure 3.3 in relation-
ship to the observed TOC concentrations. Concentrations of free su If ides
in Commencement Bay surface sediments indicated in Figure 3.3 were classified
as either <10 or >_10 mg/kg DW. This general classification of sediments
into groups of "low" and "high" sulfide content takes into account uncertainty
in analytical results for most of the sulfide analyses performed (see preser-
vation discussion in Methods, Section 2.2). The sulfide values reported
for samples collected in March, 1984 are considered minimum estimates of
3.8
-------
in situ concentrations. Maximum sulfide levels were reported for preserved
sediments collected during January, 1984 and ranged up to 710 mg/kg DW
at Station CI-02.
All Commencement Bay sediments with substantial organic enrichment
(i.e., >10 percent TOC) also contained sulfides >_10 mg/kg DW, as did most
sediments with moderate organic enrichment (i.e., 5-10 percent TOC). Low
concentrations of sulfides (i.e., <10 mg/kg DW) were measured in most
Cortmencement Bay sediments with low organic enrichment (i.e., <5 percent TOC).
Reference sediments from Carr Inlet contained <6 mg/kg sulfides and <0.3 percent
TOC.
High-sulfide sediments were found throughout the organically enriched
City Waterway, except at two stations at the mouth of the waterway (Figure 3.3),
where TOC levels measured <3 percent. Sediments collected from all stations
within the adjacent Middle Waterway contained high sulfides, as did sediments
from the organically enriched Station SP-14 in St. Paul Waterway off the
main Champion International paper mill outfall. Low-sulfide sediments
were found at all other St. Paul Waterway stations and at all stations
from Milwaukee and Sitcum Waterways. Low sulfide concentrations in these
sediments coincided with relatively low TOC concentrations, an apparent
common characteristic of stations near the mouth of the Puyallup River.
With some exceptions, low sulfide levels were also found throughout Blair
Waterway, where TOC averaged <1.5 percent.
Sediment sulfide concentrations in upper Hylebos Waterway were high
in the organically enriched sediments off the Kaiser Ditch. Moderately
organically enriched sediments in the upper turning basin of Hylebos Waterway
off Hylebos Creek had consistently low sulfide concentrations. Sulfide
concentrations >10 mg/kg DW were found in several sediment samples collected
near major outfalls along Hylebos Waterway, and in some samples collected
outside the waterway mouth; most of these samples contained <5 percent TOC.
3.1.1.4 Total Volatile Solids (TVS)--
TVS measurements are often used instead of TOC measurements as a relatively
inexpensive means of testing for organic enrichment. TVS is determined
by the difference in the total weight of a sediment sample before and after
heating at >_550° C. This technique is less precise than the quantitative
determination of TOC in a sample by combustion, and can overestimate the
actual organic load because of simultaneous volatilization of inorganic
sediment components with organic carbon and non-carbon organic material.
The amount of volatilized inorganic components will vary among sediments.
Despite these potential limitations, a strong correlation was found
in the overall distribution of percent TVS with percent TOC in sediments
from Commencement Bay and Carr Inlet. The linear regression equation determined
for these data is:
TOC = -0.346 + 0.5051(TVS) r? = 0.81, n=144
The regression predicts that TOC is approximately half the observed TVS
value, or that TVS overestimates TOC by approximately a factor of two.
The variability in the average ratio of percent TVS to TOC among Commencement
3.9
-------
Bay study areas is demonstrated in Figure 3.4. The greatest variability
in this ratio, approaching 100 percent, was found for sediments from the
Ruston-Pt. Defiance Shoreline. The average ratio varied among study areas
by a factor of approximately three. There was no consistent trend among
study areas between TVS/TOG variation and grain size differences shown
in Figure 3.1, although a high average ratio of TVS to TOC was observed
for coarse sediments from the Ruston-Pt. Defiance Shoreline and from Carr
Inlet. TVS/TOC ratios exceeding an order of magnitude were found at two
stations: HY-46 in lower Hylebos Waterway and RS-13 along the Ruston-Pt.
Defiance Shoreline (ratio of 15 and 13, respectively).
The overall strong correlation of TVS with TOC observed for Commencement
Bay and Carr Inlet sediments suggests that TVS is a valuable indicator
of organic enrichment for general purposes. Because of the range and
variability in the ratio of TVS to TOC among sediments, direct measurements
of TOC are used in this report when calculating chemical concentrations
normalized to sediment organic content for use in source and biological
effects evaluations (see discussion below in Section 3.1.2).
3.1.1.5 Total Organic Carbon/Nitrogen Ratios (C/N)--
The average ratio of carbon to nitrogen (C/N) for study area sediments,
after correction for differences in the atomic weight of the two molecules,
is given in Figure 3.5. Elevated sediment C/N ratios, which provide evidence
that carbon-rich materials have been incorporated into the sediments, have
been used as a general indicator of sediment contamination. Examples of
sources of this material in urban discharges include coals, oils, and paper
products. Sewage effluents contain substantial loads of carbon-rich material
(e.g., cellulose), but are also nitrogen-rich. Therefore, although an
elevated C/N ratio is indicative of contamination, a lower C/N ratio is
not proof that a sediment is contaminant-free.
The observed average atomic C/N ratio for Carr Inlet sediments (i.e., 8.5)
is typical of marine sediments. The average atomic C/N ratio for sediments
in all Commencement Bay study areas is substantially higher than reference.
These data suggest that carbon-rich materials have accumulated over most
of the Commencement Bay area. This is true even for sediments from some
stations located outside of the mouths of Hylebos and Blair Waterways,
where atomic C/N ratios ranged from 1.3 to 20. Aside from local discharges,
a source of carbon-rich material in Commencement Bay sediments is accumulations
of Puyallup River particulate material, which likely contains coal fragments
eroded from upriver deposits (Barrick et al. 1984).
3.1.2 Normalization of Chemical Concentrations
In this report, chemical data are used to:
• Determine the relative magnitude of contamination among
Commencement Bay areas and in comparison with reference
conditions at Carr Inlet
t Define areas with problem sediments, where sediment toxicity
or biological effects are shown to occur above some threshold
concentration of a chemical in sediments
3.10
-------
• Evaluate spatial and temporal distributions of contaminants
when tracing potential sources of contamination (heavily
contaminated areas will be prioritized for possible source
control even if no clear relationship to observed sediment
toxicity or biological effects has been established).
To accomplish these objectives, chemical data must be normalized to
account for physical and physicochemical differences among samples. Otherwise,
these differences may mask potential trends in chemical concentrations
that would be useful in interpreting environmental data. Sediment chemical
concentrations in this report are expressed in three possible ways, as
appropriate: the mass of a chemical relative to (1) total sediment dry-weight,
(2) total weight of the fine-grained sediment fraction, or (3) total weight
of sediment organic carbon. These normalizations are based on observed
and theoretical factors known to affect the quantity of chemicals in a
given volume of sediment:
1. Most sediment contaminants are associated primarily with
the solid material in bulk sediments, not with the interstitial
water. Because the percent water content can vary considerably
among samples, wet-weight concentrations are typically poor
indicators of the relative quantity of chemicals among samples.
2. Fine-grained sediments naturally tend to accumulate more
chemicals than coarse-grained sediments because the relative
surface area available for adsorption of chemicals increases
with decreasing grain size.
3. Many trace chemicals are associated and transported with
organic carbon-rich particles in the environment, or can
be bound by organic carbon in sediments. Carbon-rich sediments
tend to contain a larger quantity of these chemicals than
carbon-poor sediments.
The first major use of chemical data in this report is to evaluate
the relative magnitude of contamination among Commencement Bay areas.
Dry-weight concentrations were selected for this evaluation. Changes in
dry-weight concentrations reflect proportional changes in the relative
quantity of chemicals at different sites because the bulk dry density of
sediment is nearly constant at approximately 2.5 g/cm3 pn situ; Robbins
and Edgington 1975), regardless of variations in the grain size distribution.
For example, 10 mg of copper measured in a sample containing 80 percent
sand would yield approximately the same dry-weight concentration as 10 mg
of copper measured in an equal volume of sample containing 80 percent clay.
The magnitude of error associated with the assumption of equal density
among Commencement Bay sediments is probably less than 50 percent, given
the natural variability in densities of common expandable clays (e.g.,
montmoril linite) and differences in densities attributable to enrichment
of slag particles, for example, in some bulk sediments.
A comparison of contamination among Commencement Bay sites with reference
conditions at Carr Inlet is also made on a dry-weight basis in later sections.
Data presented in Figure 3.1 indicate that much coarser sediments are found
3.11
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in Carr Inlet than in most of Commencement Bay. For the reasons just stated,
comparisons of dry-weight concentrations between the two areas provide
a reasonable estimate of the relative mass of contaminants in fine-grained
Corrmencement Bay sediments compared with those in the coarse-grained sediments
at Carr Inlet. Differences in average grain size distributions are relevant
in interpreting the significance of observed elevations in dry-weight
concentrations. Because of the lower capacity of sandy sediments to accumulate
and transport pollutants relative to fine-grained sediments, elevated
contaminant levels within sandy sediments would not be expected, except
at sites directly adjacent to a contaminant discharge. The meaning of
a "significant" elevation above reference for dry-weight concentrations
is presented in Section 3.1.3 (Sediment Metals) and Section 3.1.4 (Sediment
Organic Compounds).
The second major use of chemical data in this report is to evaluate
relationships among chemical concentrations, sediment toxicity, and biological
effects to help define action levels. Only a small portion of the total
amount of a contaminant may be bioavailable (i.e., available for direct
contact with organisms either through surface contact, respiration, or
ingestion). The bioavailable portion of the total contaminant mass may
also vary among sediments. Hence, measurements of the total sediment
concentration of a chemical may not correspond with changes in observed
toxicity or biological effects among different sediment samples. Sediment
matrix effects that alter the bioavailability of contaminants include adsorption
of chemicals onto sediment surfaces and absorption into sediment matrices
[e.g., fecal pellets (Karickhoff and Morris 1985), humic substances, or
clay lattices]. An increase in organic carbon content, sediment surface
area, or expandable clay content may result in contaminants being bound
to particles in such a way that the bioavailability of the contaminant
is reduced.
For example, a coarse-grained sediment with a low dry-weight concentration
of a toxic contaminant and a fine-grained, organic-rich sediment with a
high dry-weight contaminant concentration may exhibit similar toxicity.
When normalized to organic carbon or percent fine-grained material, the
resulting normalized concentrations may be similar, thus supporting the
observed similarity in toxicity. This situation would suggest that similar
available or effective amounts of a contaminant were present in the two
dissimilar bulk sediment samples. The bioavailability question may be
resolved by direct measurements of contaminant concentrations associated
with different sedimentary components (e.g., interstitial water, or a specific
size or density fraction of the sediment). These tests were beyond the
scope of the present study. Therefore, the approach here is to examine
whether increases in observed toxicity or biological effects correspond
with increased contaminant concentrations of metals and/or organic compounds
after normalization to organic carbon or percent fine-grained material.
The third major use of chemical data in this report is to identify
potential sources of contamination. For organic compounds, these source
identifications make use of trends in sediment concentrations normalized
to dry weight and to total organic carbon content. Interpretation of trends
in metal concentrations are based on dry weight and normalizations to the
total weight of the fine-grained sediment fraction (>4 phi). Inorganic
and organic chemicals from pollution sources tend to be selectively enriched
3.12
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in sediment participate fractions having a high content of hydrous manganese
or iron oxides, high surface area, high organic carbon content, or low density
(e.g., Lerman 1979; Thompson and Eglinton 1978; Karickhoff et al. 1979;
Prahl and Carpenter 1983). Dilution of chemically enriched sediment fractions
with variable amounts of unrelated material during transport and deposition
can distort spatial trends when interpreted on the basis of dry-weight
concentrations. Organic carbon or fine-grained sediment normalizations
are used primarily to factor out this variability in bulk sediments when
patterns in dry-weight concentrations are not apparent. When a clear gradient
in dry-weight concentrations is apparent, further normalizations of chemical
concentrations may be unnecessary to trace potential sources. In these
cases, organic carbon or fine-grained sediment normalizations can be used
to establish whether the major carbon or fine-grained sediment source in
the area coincides with the source of contaminants. For example, a strong
gradient in dry-weight concentrations that disappears after normalization
to organic carbon suggests that the pollutant source is also a major source
of organic carbon. The actual loading of contaminants on the organic carbon
may be no different than that in some other area with lower dry-weight
concentrations. Alternatively, a strong gradient in dry-weight concentrations
that reverses or intensifies after normalization to organic carbon suggests
that the discharge contributes to increased loadings of contaminants on
the sedimentary organic carbon derived from a separate source.
No single concentration normalization is used in this report to the
exclusion of others that may offer complementary information. Because
organic carbon or fine-grained material in sediments have a finite capacity
to bind contaminants and potentially reduce their bioavailability, sediments
that are highly contaminated based on dry-weight and other normalizations
are of greatest concern. Conversely, sediments with low contamination
regardless of the normalization used are of lowest concern.
3.1.3 Sediment Metals
3.1.3.1 Surface Sediments--
Ranges in concentrations (dry weight, DW) of 16 elements in surface
subtidal sediments from Conmencement Bay and Carr Inlet are shown in Table 3.1.
These elements include the 13 U.S. EPA priority pollutant metals. Three
of these "metals" (antimony, arsenic, and selenium) are classified as
metalloids, which are elements that do not strictly occur as metals in
the environment. Following U.S. EPA convention and for ease of discussion,
all of these elements will be referred to as metals.
The results include data for two 1984 sediment surveys conducted as
part of the Superfund investigation. Additional data are included from
1984 for the Blair Waterway Dredging Survey conducted as a combined effort
between the Port of Tacoma and this Commencement Bay Superfund project.
In addition to the U.S. EPA priority pollutant metals, distributions of
iron and manganese were determined to enable a comparison of levels of
predominantly naturally derived metals among stations. Iron and manganese
also form oxides that are important scavengers affecting the distribution
of other metals. Barium concentrations were measured to evaluate if EP
(Extraction Procedure) toxicity tests for barium would be required for
sediments potentially requiring disposal as hazardous waste.
3.13
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Most metals were detected in all samples. Highest concentrations
of metals were found along the Ruston-Pt. Defiance Shoreline. The distributions
of metals that were frequently detected over a range of concentrations
or that were found in high concentration at a few sites are discussed in
Section 3.1.5. The remaining metals (i.e., selenium, thallium) were either
undetected at the detection limits stated in Table 3.1, or were rarely
found in high dry-weight concentrations (i.e., beryllium, sliver). Their
distributions are summarized in this section and these metals will not
be discussed further.
Beryllium was detected at most sites, but its distribution was relatively
uniform and concentrations did not exceed 0.6 mg/kg DW. Highest beryllium
concentrations were found in Hylebos Waterway and near the major outfalls
of the ASARCO plant on the Ruston-Pt. Defiance Shoreline. Selenium and
thallium concentrations in sediments sampled directly off the major outfalls
of the ASARCO plant were elevated over an order of magnitude above typical
Commencement Bay levels. Selenium was undetected at all other sites and
thallium was not present at more than twice its detection limit (0.05 mg/kg DW)
at any other site. Silver concentrations did not exceed 0.6 mg/kg DW,
except in sediments collected in January, 1984 from two City Waterway stations
(CI-02, CI-03) where concentrations exceeded 2 mg/kg DW. Subsequent sampling
at nearby stations in March, 1984 did not show similar levels.
3.1.3.2 Subsurface Sediments--
Twenty-three sediment box or gravity cores of 1-6 ft (0.3-1.8 m) in
length were analyzed from Hylebos, Sitcum, St. Paul, Middle, and City Waterways,
and from the Ruston-Pt. Defiance Shoreline. These cores were collected
at 18 stations in 13 areas where contaminated surface sediments were found.
Additional cores of up to 8 ft (2.4 m) in length were collected using a
drilling rig at 17 sites in Blair Waterway as part of a combined effort
between the Port of Tacoma and this Commencement Bay Superfund project.
Ranges in concentrations (DW) of inorganic chemicals analyzed in composited
sediments from different core depths are summarized in Table 3.2. Maximum
subsurface and surface sediment concentrations can be used to compare extreme
historical and present conditions. A comparison of mean subsurface values
with mean surface values from throughout the study area was not made because
cores were collected only in areas where substantial contamination by inorganic
or organic substances was indicated in surface sediments; surface sediments
were collected from multiple sites ranging from low to high contamination.
Maximum subsurface concentrations of most elements were higher by
factor of 1.5 to 3 times the maximum surface concentrations reported in
Table 3.1. These maximum subsurface and surface sediment concentrations
almost always occured in cores from along the Ruston-Pt. Defiance Shoreline.
Maximum iron and manganese concentrations in subsurface and surface sediments
from this area also fell within this range of differences. These elements
are derived from predominantly natural sources that have presumably been
reasonably constant over time, although natural variability in accumulations
over time and among different sediment types is expected. Therefore, the
observed differences may be related to natural variability in sediment
deposition, not to a major change in the discharge of metals from pollutant
sources. Concentrations of metals (e.g., lead and copper) also did not
3.14
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TABLE 3.1. CONCENTRATIONS OF U.S. EPA PRIORITY POLLUTANT TRACE METALS
AND ADDITIONAL METALS IN SURFACE SEDIMENTS (0-2 cm)
FROM COMMENCEMENT BAY AND CARR INLET
Antimony
Arsenic
Barium
Beryllium
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Mercury
Nickel
Selenium
Silver
Thallium
Zinc
Range
(mg/kg dry wt)
U 0.10&- 420
2.4 - 12,000
5.1 - 150
U 0.02 - 0.55
U 0.1 - 180
5.4 - 62
4.9 - 14,000
6,200 - 120,000
4.4 - 6,200
55 - 750
0.01 - 52
6.9 - 350
U 0.05 - 26
0.02 - 2.4
U 0.10 - 3.2
15 - 4,200
Detection
Frequency3
142/148
148/148
129/129
145/148
144/148
148/148
148/148
148/148
148/148
148/148
147/148
147/147
12/148
138/148
19/148
148/148
Location
of
Maximum
RS-18
RS-17
RS-21
RS-21
RS-18
CI-02
RS-21
RS-21
RS-18
RS-18
RS-18
RS-21
RS-17
CI-02
RS-18
RS-21
a Detection frequency includes replicate samples; maximum of 10 percent
replication. Original data listed in Appendix IV.
b U: Undetected at the detection limit shown.
3.15
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TABLE 3.2. U.S. EPA PRIORITY POLLUTANT TRACE METALS AND ADDITIONAL
METALS IN SUBSURFACE SEDIMENTS FROM COMMENCEMENT BAY
Range
(mg/kg dry wt)
Antimony
Arsenic
BariumC
Beryllium
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Mercury
Nickel
Selenium
Silverc
Thallium
Zincc
U O.lb-
1.4 -
9.2 -
U 0.05 -
U 0.10 -
8.9 -
10 -
8,700 -
U 2.0 -
63.0 -
U 0.04 -
0.36 -
U 0.05 -
U 0.05 -
U 0.1 -
18 -
200
30,000
460
1.0
280
130
36,000
190,000
10,000
1,900
21
930
26
18
2.0
13,000
Detection
Frequency3
93/130
130/130
129/130
114/130
81/130
130/130
130/130
130/130
125/130
130/130
98/129
130/130
8/130
77/130
6/130
130/130
Location
of
Maximum
RS-61-H3
RS-62-H1
RS-61-H3
RS-61-H1
RS-61-H1
RS-61-H1
RS-61-H1
RS-61-H1
RS-61-H1
RS-61-H1
RS-62-H2
RS-61-H1
RS-62-H2
RS-60-H1
RS-61-H1
RS-61-H5
a Detection frequency includes replicate samples; maximum of 10 percent
replication. Original sample data listed in Appendix IV.
b U: Undetected at the detection limit shown.
c Ratios of maximum observed subsurface to surface concentrations were
greater than three for only the following metals: barium (ratio 3.1);
silver (ratio 7.5); zinc (ratio 3.1).
3.16
-------
vary substantially with depth in cores from Wheeler-Osgood Waterway, the
middle of the main channel of City Waterway, and St. Paul Waterway.
All metal concentrations (DW) in the bottom interval analyzed from
cores drilled in Blair Waterway were comparable to Puget Sound reference
conditions (see Section 3.1.3.3). Similarly low metal concentrations were
found in the bottom interval of box or gravity cores from four stations
in Hylebos Waterway (cores HY-60, HY-60A, HY-61, and HY-62; Figure 2.3).
Concentrations of metals at the bottom of four cores were within a factor
of two of Puget Sound reference conditions (HY-63A, CI-60, CI-62, and SP-
60). Concentrations of at least one metal in the bottom of 11 other cores
were greater than two times maximum Puget Sound reference conditions (cores
CI-61, CI-63, HY-60B, HY-63, HY-63B, HY-63C, MO-60, RS-60, RS-61, RS-62,
and SI-60).
3.1.3.3 Sediment Metals of Concern--
The range of trace metal concentrations in sediments from Puget Sound
reference areas are summarized in Table 3.3. It is assumed that the range
of reference concentrations provides a reasonable measure of the possible
variability in concentrations in relatively uncontaminated sediments.
Eight metals are of concern because their concentrations (DW) in Commencement
Bay surface sediments exceeded the range of concentrations for Puget Sound
reference areas. These metals of concern are listed in Table 3.4. Areas
containing the most contaminated sediments are also summarized in the table.
Distributions of these elements within Commencement Bay study areas and
their relative importance in problem areas are discussed in Section 6.
Concentrations of beryllium, chromium, and silver in Commencement
Bay surface sediments were within the ranges observed in Puget Sound reference
areas. Thus, there is no evidence that surface subtidal sediments in
Commencement Bay are contaminated by these three elements above reference
conditions and they have not been defined as metals of concern. Silver
was found to be elevated above reference conditions in at least one interval
of cores from Stations CI-60, CI-61, HY-60B, RS-60, RS-62, and SI-60.
Therefore, sediments contaminated with silver may be exposed during dredging
operations in these areas. Beryllium and chromium concentrations did not
exceed the range of Puget Sound reference conditions in any subsurface
sample.
Except for stations directly off ASARCO plant outfalls on the Ruston-
Pt. Defiance Shoreline, surface and subsurface sediments in Commencement Bay
do not appear to be contaminated by selenium or thallium at levels that
exceed Puget Sound reference conditions. Given this distribution, selenium
and thallium are not classified as chemicals of general concern. High
concentrations of barium were found in sediments from a few stations along
the Ruston-Pt. Defiance Shoreline, at levels ranging from 10 to 22 times
reference conditions. Barium concentrations in the remaining Commencement Bay
study areas ranged from 2 to 8 times reference values (available only from
Carr Inlet). Optimal procedures for the efficient digestion of barium
salts were not available. Hence, the concentrations reported may underestimate
the total in both Commencement Bay and Carr Inlet sediments. However,
there are no known major sources of barium in the region and barium is
not defined as a contaminant of general concern.
3.17
-------
TABLE 3.3. SUMMARY OF METAL CONCENTRATIONS IN
SEDIMENTS FROM PUGET SOUND REFERENCE AREAS
Range
(mg/kg dry wt)
Antimony
Arsenic
Beryllium
Barium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Silver
Thallium
Zinc
U O.lb-
1.9 -
0.07 -
5.6 -
0.1 -
9.6 -
5 -
U 0.1 -
0.01 -
4 -
U 0.1 -
0.02 -
U 0.1 -
15 -
1.7
17
5.5
7.8
1.9
130
74
24
0.28
47
1.0
3.3
0.2
100
Mean
(mg/kg dry wt)
0.32C - 0.38
-------
TABLE 3.4. COMPARISON OF THE RANGE IN ELEVATIONS
ABOVE REFERENCE (EAR) FOR INORGANIC CONTAMINANTS OF CONCERN
IN SURFACE SEDIMENTS (0-2 cm) FROM COMMENCEMENT BAY
Antimony
Arsenic
Cadmium
Copper
Lead
Mercury
Nickel
Zinc
0.5
1.6
0.1
1.7
0.9
0.9
0.4
1.1
Elevation
Range
- 2,300
- 3,600
- 190
- 2,200
- 680
- 1,200
20
- 220
Above
Median
6.0
7.3
2.4
13
7.3
5.0
0.9
5.0
Reference3
Threshold**
9.3
5.0
2.0
12
2.6
6.5
2.7
5.3
Areas Where
Sediments
Exceeded
lOx
Threshold0
RS,HY
RS.HY
RS
IS
RS,CI,MD,SI
RS,HY,MD
none RS
RS
a Dry-weight concentration in Commencement Bay sediments divided by the
average concentration measured in six Carr Inlet reference sediments.
b The threshold EAR is defined as the ratio of the maximum reference sediment
concentration in Puget Sound divided by the average for six Carr Inlet
reference sediments. Above the threshold EAR, the dry-weight concentration
of a Commencement Bay sediment contaminant would exceed the maximum concentra-
tion (or detection limit) reported for any Puget Sound reference site listed
in Table 3.3.
c The contaminant EAR in sediments from at least one station in each area
listed exceeded the threshold level indicated by an order of magnitude.
Sediments in underlined areas had the highest observed values. "None"
indicates that no sediment analyzed from Commencement Bay study areas exceeded
the threshold by an order of magnitude. The area with the highest value
is still listed.
3.19
-------
3.1.4 Sediment Organic Compounds
3.1.4.1 Surface Sediments--
Ranges in concentrations (DW) for the 133 U.S. EPA organic priority
pollutant and additional hazardous substance list compounds analyzed in
Commencement Bay and Carr Inlet surface subtidal sediments are summarized
in Table 3.5. These results include data for the 1984 Blair Waterway Dredging
Survey in which similar analytical methods were used. Ranges in concentrations
for an additional 14 tentatively identified compounds specifically searched
for in GC/MS analyses of surface sediments are presented in Table 3.6.
Most of these latter compounds were not analyzed for in the Blair Waterway
Dredging Survey. Organic compounds in tables used in this report are grouped
with other chemically related compounds and, except for pesticides, are
listed in order of increased structural complexity within each group.
Structures and molecular weights of all compounds discussed are shown in
Appendix I.
The most frequently detected organic compounds in sediment samples
were aromatic hydrocarbons containing one to six rings. The distributions
of these and other compounds that were frequently detected or were detected
at high concentrations at a few sites are summarized in Section 3.1.5.3.
Fifty-three compounds were undetected in all surface sediments at
the detection limits summarized in Table 3.5. Special analyses were conducted
for 2,3,7,8-tetrachlorodibenzo-p-dioxin in 32 sediment samples. Dioxin
was undetected at a detection limit of <0.3 ug/kg DW in all cases. Additional
undetected substances include most of the organonitrogen compounds (bases),
pesticides, and volatile compounds. Volatile compounds were analyzed for
at only 20 stations, however. Compounds that were only detected a few
times at low concentrations (i.e., <10 ug/kg DW) include several substituted
phenols and halogenated ethers. It cannot be determined if these 53 compounds
contribute to observed sediment toxicity or biological effects if they
are present at concentrations below the low part per billion detection
limits attained. Within the scope of the Superfund investigation, these
compounds do not appear to be of major concern for Commencement Bay.
Pesticides were analyzed by GC/MS in all sediment samples except those
analyzed in the Blair Waterway Dredging Survey, which were analyzed by
electron capture gas chromatography (EC/GC). The GC/MS technique is less
sensitive than pesticide analysis by EC/GC, but provides positive confirmation
of compound identifications. Interfering substances can result in false
identifications using EC/GC. By using GC/MS, less sensitive pesticide
detection limits were attained than in most historical analyses for Commencement
Bay, all conducted using EC/GC. However, there were no confirmations of
the high historical concentrations in intertidal and subtidal sediments
summarized by Johnson et al. (1983) (i.e., on the order of hundreds of
ug/kg DW for pesticides such as aldrin, lindane, or DDT). The only pesticide
detected and confirmed by GC/MS identification was DDT at Station CI-01
(50 ug/kg DW). It appears that the previous EC/GC reports of substantial
pesticide contamination in some study areas are incorrect, or at least
no longer apply to current sediment conditions. Recent pesticide analyses
using EC/GC reported for the 1984 Blair Waterway Dredging Survey are included
3.20
-------
TABLE 3.5. CONCENTRATIONS OF U.S. EPA ORGANIC PRIORITY POLLUTANTS AND
ADDITIONAL HAZARDOUS SUBSTANCE LIST (HSL) COMPOUNDS IN SURFACE
SEDIMENTS (0-2 cm)
Phenols (acids; 4)
65& phenol
HSL 2-methyl phenol
HSL 4-methyl phenol
34 2,4-dimethylphenol
Substituted Phenols (acids;
24 2-chlorophenol
31 2,4-dichlorophenol
22 4-chloro-3-methyl phenol
21 2,4,6-trichlorophenol
HSL 62,4,5-trichlorophenol
64 pentachlorophenol
57 2-nitrophenol
59 2,4-dinitrophenol
60 4,6-dinitro-o-cresol
58 4-nitrophenol
Low Molecular Weight Aromatic
55 naphthalene
HSL 2-methylnaphthalene
77 acenaphthylene
1 acenaphthene
80 fluorene
81 phenanthrene
78 anthracene
FROM COMMENCEMENT BAY AND CARR INLET
Range Detection
(ug/kg dry wt) Frequency^
U 1.0C- 2,100 134/158
U 0.6 - 100 72/143
U 1.0 - 96,000 114/143
U 0.5 - 210 36/158
10)
0.1 - U 25 8/158
0.1 - U 50 12/158
0.1 - U 50 3/158
0.2 - 160 12/158
U 10 - 150 2/126
0.1 - 860 45/158
0.1 - U 50 10/158
U 0.5 - U 190 0/32
U 0.5 - U 500 0/158
U 0.5 - U 1,900 3/158
Hydrocarbons (neutrals; 7)
U 0.5 - 5,500 153/158
1.0 U - 1,200 146/156
U 0.5 - 650 149/158
U 0.5 - 2,500 147/158
0.5 - 3,100 151/157
2 - 11,000 157/157
U 0.5 - 1,600 155/157
Location
of
Maximum
HY-16
SP-13
SP-14
RS-16
d
d
d
HY-31
MD-11
BL-30
d
undetected
undetected
Bll
CI-12
RS-18 &
CI-02
CI-21
RS-18
RS-18
RS-18
CI-21
High Molecular Weight Aromatic Hydrocarbons (neutrals; 10)
39 fluoranthene
84 pyrene
72 benzo(a) anthracene
76 chrysene
74 benzo(b) fluoranthene
75 benzo(k) fluoranthene
73 benzo(a) pyrene
83 indeno(l,2,3-c,d)pyrene
82 dibenzo(a,h)anthracene
79 benzo(g,h,i)perylene
11 - 8,100 158/158
11 - 5,800 158/158
4 - 3,500 155/156
U 5 - 6,100 155/156
RS-18
HY-19
HY-19
HY-16
Combined with benzo(k)fluoranthene
U 5 - 8,800 135/136
3 - 6,100 154/156
U 0.5 - 2,700 148/157
0.4 - 1,500 137/157
U 0.5 - 1,900 147/157
HY-16
HY-22
HY-22
HY-22
HY-16
3.21
-------
TABLE 3.5. (Continued)
Chlorinated Aromatic Hydrocarbons (
26 1,3-dichlorobenzene
27 1,4-dichlorobenzene
25 1,2-dichlorobenzene
8 1,2,4-trichlorobenzene
20 2-chloronaphthalene
9 hexachlorobenzene (HCB)
Chlorinated Aliphatic Hydrocarbons
12 ehexachloroethane
xx trichlorobutadiene isomers
xx tetrachlorobutadiene isomers
xx pentachlorobutadiene isomers
52 hexachlorobutadiene
53 ehexachlorocyclopentadiene
Halogenated Ethers (neutrals; 5)
18 bis(2-chloroethyl) ether
42 bis(2-chloroisopropyl) ether
43 bis(2-chloroethoxy)methane
40 4-chlorophenyl phenyl ether
41 4-bromophenyl phenyl ether
Phthalates (neutrals; 6)
71 dimethyl phthalate
70 diethyl phthalate
68 di-n-butyl phthalate
67 butyl benzyl phthalate
66 bis(2-ethylhexyl)phthalate
69 di-n-octyl phthalate
Miscellaneous oxygenated compounds
54 isophorone
HSL benzyl alcohol
HSL benzoic acid
129 2,3,7,8-tetrachlorodibenzo-
p-dioxin
HSL dibenzofuran
neutrals; 6)
U 0.5 -
U 0.5 -
0.1 -
U 0.5 -
U 0.5 -
0.2 -
(neutrals; 3
U 0.5 -
U 0.5 -
U 10 -
U 10 -
U 0.5 -
U 0.5
0.2 -
U 0.5 -
U 0.5 -
U 0.5 -
U 0.5 -
B 0.5C-
B 0.5 -
B 0.5 -
U 0.5 -
210
290
350
260
U 25
730
plus CBD
2,800
43,000
18,000
3,600
940
U 50
U 400
91
U 25
U 25
1,100
120
9,800
890
B 0.5 -G 8,000
U 0.5 -
(neutrals; 5)
U 0.5 -
U 10 -
U 1.0 -
U 0.3 -
U 1.0 -
420
U 130
500
8,000
U 0.2
2,000
57/158
104/158
47/158
25/158
0/158
34/158
isomers)
4/158
54/145
84/145
46/145
33/158
0/18
4/158
1/158
1/140
0/158
0/158
78/157
37/157
94/157
51/150
61/157
33/155
13/157
87/126
63/143
0/32
131/143
BL-19
HY-31
CI-11
CI-16
HY-46 &
HY-22
undetected
HY-22
HY-22
HY-46
HY-46
HY-46
HY-46
undetected
d
d
B-14
undetected
undetected
HY-21
HY-48
CB-11
HY-35
CI-02
B-09
d
HY-21
BL-16
undetected
RS-18
3.22
-------
TABLE 3.5. (Continued)
Organonitrogen Compounds (bases; 13}
HSL aniline
56 nitrobenzene
63 n-nitroso-di-n-propylamine
HSL 4-chloroaniline
HSL 2-nitroaniline
HSL 3-nitroaniline
HSL 4-nitroam"line
36 e2,6-dinitrotoluene
35 2,4-dinitrotoluene
62 n-nitrosodiphenylamine
37 el,2-diphenylhydrazine
5 benzidine (4,4'-diaminobipheny1)
28 3,3'-dichlorobenzidine
U 1.0
U 0.5
U 0.5
U 50
U 50
U 50
U 50
U 0.5
U 0.5
0.2
U 0.5
U 0.5
U 0.5
- 1,400
- U 25
- U 50
- U 250
- U 250
- U 250
- U 250
- U 50
28
- 610
- 1,200
- U 500
3/143
2/157
2/151
0/126
0/126
0/126
0/126
8/157
3/157
31/157
4/158
0/13
0/139
CI-11
d
d
undetected
undetected
undetected
undetected
d
CI-01
RS-18
BL-12
undetected
undetected
Pesticides (neutrals; 18)
93 p,p'-DDE
94 p.p'-DDD
92 ep,p'-DDT
89 aldrin
90 dieldrin
91 chlordane
95 alpha-endosulfan
96 beta-endosulfan
97 endosulfan sulfate
98 endrin
99 endrin aldehyde
100 heptachlor
101 heptachlor epoxide
102 alpha-HCH
103 beta-HCH
104 delta-HCH
105 gamma-HCH (lindane)
113 toxaphene
U 0.01- U
U 0.03- U
U 0.01- U
U 0.01- U
U 0.01- U
U 10 - U
U 0.02- U
U 0.03- U
U 0.03- U
U 0.03- U
U 0.02- U
U 0.02- U
U 0.02- U
U 0.01- U
U 0.03- U
U 0.02- U
U 0.01- U
U 10 - U
50
50
50
50
50
50
50
50
50
50
50
50
50
50
50
50
50
22
5/157
4/158
11/158
1/158
0/158
0/158
0/157
0/157
0/157
0/158
0/157
1/158
0/158
0/158
0/158
0/158
0/158
0/32
d
d
d
d
undetected
undetected
undetected
undetected
undetected
undetected
undetected
d
undetected
undetected
undetected
undetected
undetected
undetected
PCBs (neutrals; used as total PCBs only)
xx Total PCBs (primarily 1254/1260) 4 - 2,000
113/144
HY-22
3.23
-------
TABLE 3.5. (Continued)
Volatile Halogenated Alkanes (neutrals; 17)
dichlorodifluoromethane (removed)
45 chloromethane
46 bromomethane
16 chloroethane
44 methylene chloride (dichloromethane)
fluorotrichloromethane (removed)
13 l,l'-dichloroethane
23 echloroform
10 1,2-dichloroethane
11 1,1,1-trichloroethane
6 carbon tetrachloride
48 bromodichloromethane
32 1,2-dichloropropane
51 chlorodibromomethane
14 1,1,2-trichloroethane
47 bromoform
15 1,1,2,2-tetrachloroethane
Volatile Halogenated Alkenes (neutrals;
88 vinyl chloride
29 l,l'-dichloroethene
30 trans-l,2-dichloroethene
33 cis and trans-l,3-dichloropropene
87 trichloroethene
85 tetrachloroethene
Volatile Aromatic Hydrocarbons (neutrals; 5)
u
u
u
u
u
u
u
u
u
u
u
u
u
u
u
u
6)
u
u
u
u
u
u
10
10
5
5
10
5
1.0
5
5
5
5
5
5
5
5
5
5
5
1.1
5
5
5
- U
- U
- U
- U
- U
- U
- U
- U
- U
- U
-
- U
- u
- u
- u
- u
- u
- u
10
10
10
10
10
10
10
10
10
10
38
10
10
10
10
10
10
10
- 210
4 benzene
86 toluene
38 ethylbenzene
HSL styrene (ethenylbenzene)
HSL total xylenes
U 0.15- U 10
U 0.19- U 10
U 0.08- 50
U 20
U 20 - 160
0/21
0/21
0/36
0/36
0/21
0/36
3/36
0/36
0/36
0/36
0/36
0/36
0/36
2/36
0/36
0/36
0/36
1/36
1/36
0/36
0/36
11/36
4/36
3/36
11/36
10/21
Volatile Chlorinated Aromatic Hydrocarbons (neutrals; 1)
7 chlorobenzene U 5 - U 10 0/36
Volatile Unsaturated Carbonyl Compounds (base/neutrals; 2)
0/21
0/21
Volatile Ethers (neutrals; 2)
2 acrolein (an unsaturated aldehyde) U 100
3 acrylonitrile (an unsaturated
nitrile) U 100
bis(chloromethyl)ether
19 2-chloroethylvinyl ether
U 5 - U 100
undetected
undetected
undetected
undetected
not reported
undetected
undetected
d
undetected
undetected
undetected
undetected
undetected
undetected
B-ll
undetected
undetected
undetected
d
d
undetected
undetected
HY-17
d
d
HY-17
undetected
HY-17
undetected
undetected
undetected
not analyzed
undetected
3.24
-------
TABLE 3.5. (Continued)
Volatile Ketones (neutrals; 4)
HSL acetone U 20 0/20 undetected
HSL 2-butanone U 20 0/20 undetected
HSL 2-hexanone U 20 0/20 undetected
HSL 4-methyl-2-pentanone U 20 0/20 undetected
Miscellaneous Volatile Compounds (neutrals; 2)
HSL carbon disulfide 5 - U 10 9/20 d
HSL vinyl acetate U 20 0/20 undetected
a Detection frequency includes replicate samples; maximum of 10 percent
replication. Original sample data listed in Appendix V.
b Indicates U.S. EPA priority pollutant number.
c Qualifiers -
B: Value corrected for blank contributions down to the detection
limit shown.
E: Estimated value.
G: Estimated value is greater than the minimum shown.
N/R: Not reported.
U: Undetected at the detection limit stated (ug/kg or ppb dry weight
sediment).
Z: Value corrected for blank contributions; resulting value still
exceeds the detection limit.
d Compound detected at concentration between the minimum and maximum detection
limits shown at a few stations only.
e Compounds detected only under special circumstances and were not included
in routine statistical analyses of surface sediments.
3.25
-------
TABLE 3.6. CONCENTRATIONS OF TENTATIVELY IDENTIFIED COMPOUNDS
IN SURFACE SEDIMENTS (0-2 cm) FROM COMMENCEMENT BAY AND CARR INLET
Range
(ug/kg dry wt)
Detection
Frequency
Location
of Maximum
Alkylated aromatic hydrocarbons
1-methyl-2-(1-methylethyl)benzene U» - 6600 104/123 SP-14
l.l'-biphenyl U - 1100 102/123 RS-18
2-methyl phenanthrene U - 2400 102/122 RS-18
1-methyl phenanthrene U - 1300 85/122 RS-18
1-methylpyrene U - 1500 86/123 HY-17
retene U - 2000 113/123 SI-15
2-methylpyrene U - 3400 93/123 HY-16
Diterpenoid hydrocarbons
isopimaradiene U - 5900 104/123 SP-14
unidentified diterpene
(possibly kaur-16-ene) U - 5200 97/123 SP-14
Substituted hydrocarbons
dibenzothiophene U - 1100 81/123 RS-18
pentachlorocyclopentane (isomer) U - 270 37/123 HY-46
Miscellaneous oxygenated compounds
2-methoxyphenol U - 3900 60/119 SP-14
9-hexadecenoic acid methyl ester U - 7300 99/123 HY-36
coprostanol
(a fecal sterol indicator) U - 2800 62/123 SP-11
a U: not found during a mass spectral search of a sample extract. Actual
detection limits for tentatively identified compounds were not assigned
in these cases.
3.26
-------
in the Table 3.2 summary. High pesticide concentrations were not found,
although DDTs were detected at <1-14 ug/kg DW in a few samples, aldrin
was reported at <1 ug/kg DW in three samples, and heptachlor was reported
in one sample at 0.8 ug/kg DW and in another at 1.5 ug/kg DW. Neither
GC/MS analysis nor a confirming EC/6C analysis using a column of differing
polarity were conducted on these samples, as required for verification
of these GC/EC results.
3.1.4.2 Subsurface Sediments--
Subsurface sediments were collected from 13 areas with contaminated
surface sediments, in addition to the more detailed sampling conducted
as part of the Blair Waterway Dredging Study (see discussion in Section
3.1.3.2). Ranges in concentrations (DW) of organic compounds analyzed
in composited sediments from different core depths are summarized in Table 3.7.
Original data for individual samples are reported in Appendix V. Data
for half of the 134 samples were derived from the 1984 Blair Waterway Dredging
Survey, although not all organic compounds listed in Table 3.7 were analyzed
for in the dredging survey.
Aromatic hydrocarbons were the most frequently detected compounds
in subsurface sediments, as they were in surface sediments. Organic compounds
with at least a fivefold difference between the maximum concentrations
in subsurface and surface sediments are indicated in Table 3.8. Ratios
of subsurface to surface concentrations (DW) are also shown. As discussed
for metals (Section 3.1.3.2), this presentation of the data is useful for
comparing maximum historical conditions with maximum current day conditions.
Compounds typically undetected or reported only occasionally at low
part per billion concentrations in surface and subsurface sediments include
nitrophenols, 2-chloronaphthalene, halogenated ethers, most organonitrogen
compounds, and pesticides. Volatile compound analyses were conducted on
only one subsurface sediment sample collected at a Hylebos Waterway site
heavily contaminated with chlorinated ethenes.
Organic compound concentrations in the bottom interval of most of
the Blair Waterway Dredging Survey drilling cores did not exceed the range
observed for Puget Sound reference sediments. Exceptions included a slight
elevation of PCB 1248 (35 ppb) at Station B-04 and occasional elevations
of individual hydrocarbons, primarily naphthalene. Hydrocarbon concentrations
in the bottom interval of all sediment box and gravity cores from other
Commencement Bay areas exceeded Puget Sound reference conditions typically
by a factor of 2-10 (in some cases, by a factor of >10). This was true
even in the bottom interval of the eight cores that had no evidence of
metals contamination.
Other organic compounds found at greater than reference levels in
the bottom interval of cores with no evidence of metals contamination included
phenol and methylated phenols, di-n-butyl, di-n-octyl and dimethyl phthalate
esters, benzyl alcohol, dibenzofuran, 1,3- and 1,4-dichlorobenzene, chlorinated
butadienes, and hexachlorocyclopentadiene. Total PCB contamination exceeding
Puget Sound reference conditions was detected in the bottom interval of
cores at three stations (CI-62, RS-62, and SP-60 at 310, 340, and 210 ug/kg DW,
respectively).
3.27
-------
TABLE 3.7. U.S. EPA ORGANIC PRIORITY POLLUTANTS AND ADDITIONAL
HAZARDOUS SUBSTANCE LIST (HSL) COMPOUNDS IN SUBSURFACE SEDIMENTS
FROM COMMENCEMENT BAY
Phenols
65C
HSL
HSL
34
phenol
2-methyl phenol
4-methyl phenol
2,4-dimethylphenol
Range Detection
(ug/kg dry wt) Frequency3
U l.Od- Z 6,100
-------
TABLE 3.7. (Continued)
82
79
dibenzo( a, h) anthracene
benzo(g,h ,i)peryl ene
U 1.0 -
U 1.0 -
4,100
8,600
111/134
120/134
HY-60A-H1
HY-60-H2
Chlorinated Aromatic Hydrocarbons
26 1,3-dichlorobenzene
27 1,4-dichlorobenzene
25 1,2-dichlorobenzene
8 1,2,4-trichlorobenzene
20 2-chloronaphthalene
9 hexachlorobenzene (HCB)
Chlorinated Aliphatic Hydrocarbons
12 hexachloroethane
xx trichlorobutadiene isomers
xx tetrachlorobutadiene isomers
xx pentachlorobutadiene isomers
52 hexachlorobutadiene
53 hexachlorocyclopentadiene
Halogenated Ethers (neutrals; 5)
18 bis(2-chloroethyl) ether
42 bis(2-chloroisopropyl) ether
43 bis(2-ch!oroethoxy)methane
40 4-chlorophenyl phenyl ether
41 4-bromophenyl phenyl ether
Phthalates
71 dimethyl phthalate
70 diethyl phthalate
68 di-n-butyl phthalate
67 butyl benzyl phthalate
66 bis(2-ethylhexyl) phthalate
69 di-n-octyl phthalate
Miscellaneous oxygenated compounds
54 isophorone
HSL benzyl alcohol
HSL benzoic acid
129 2,3,7,8-tetrachlorodibenzo-
p-dioxin
HSL dibenzofuran
Organonitrogen Compounds
HSL aniline
56 nitrobenzene
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 10
U 10
U 10
U 1.0
- 1,400
- 12,000
- 1,900
490
- U 50
- 9,500
- U 220
- 92,000
-500,000
-130,000
- 57,000
N/Rd- E950
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 1.0
U 10
U 25
- U 20
- U 2,000
- U 110
- U 10
- U 10
- 13,000
500
- Z 2,200
460
- Z 9,000
410
- U 50
330
820
35/134
46/134
20/134
21/134
0/134
17/134
1/134
27/ 71
34/ 71
22/ 71
17/134
4/ 4
0/134
1/134
3/134
1/134
0/134
93/134
49/134
76/134
78/134
88/134
55/134
3/134
25/ 71
5/ 65
3.9 - 1,700 70/ 71
U 20
U 1.0
U 40
U 10
O/ 71
0/134
CI-62-H1
CI-60-H2
CI-62-H1
HY-63-H3
undetected
HY-63-H2
HY-63B-H3
HY-63-H2
HY-63-H2
HY-63-H2
HY-63-H2
undetected
e
e
e
undetected
CI-62-H1
CI-62-H1
CI-62-H1
CI-60-H1
CI-60-H1
CI-60-H1
e
RS-61-H2
CI-60-H5
not analyzed
CI-63-H3
undetected
undetected
3.29
-------
TABLE 3.7. (Continued)
63
HSL
HSL
HSL
HSL
36
35
62
37
5
28
n-nitroso-di-n-propylamine
4-chloroaniline
2-nitroaniline
3-nitroanil ine
4-nitroaniline
2,6-dinitrotoluene
2,4-dinitrotoluene
n-nitrosodiphenylamine
1,2-diphenylhydrazine
benzidine (4,4'-diaminobiphenyl )
3,3' -dichlorobenzidine
n-nitrosodimethylamine
U
U
U
U
U
U
U
U
U
U
1
1
1
1
1
1
.0
50
50
50
50
.0
.0
.0
.0
.0
- U
- U
- U
- U
-
-
-
- 1
- U
36
100
100
100
100
53
40
230
,300
200
11/134
O/ 71
O/ 71
O/ 71
O/ 71
1/134
1/134
49/134
4/134
O/ 78
M-02-H1
undetected
undetected
undetected
undetected
B-06-H2
B-03-H1
CI-61-H1
CI-61-H1
not analyzed
undetected
not analyzed
Pesticides
93 p.p'-DDE
94 p,p'-DDD
92 p.p'-DDT
89 aldrin
90 dieldrin
91 chlordane
95 alpha-endosulfan
96 beta-endosu1fan
97 endosulfan sulfate
98 endrin
99 endrin aldehyde
100 heptachlor
101 heptachlor epoxide
102 alpha-HCH
103 beta-HCH
104 delta-HCH
105 gamma-HCH (lindane)
113 toxaphene
PCBs (used as total PCBs only)
xx Total PCBs (primarily 1254/1260) U 5.0 -17,000
Volatile Compoundsf
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
0
0
0
0
0
1
0
0
0
0
0
0
0
0
0
0
0
.01-
.03-
.03-
.01-
.01-
.1 -
.01-
.03-
.02-
.03-
.02-
.01-
.01-
.01-
.03-
.02-
.01-
12 -
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
U
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
18
87 trichloroethene
85 tetrachloroethene
19,000,000
14,000,000
28/134
22/134
14/134
2/134
2/134
2/134
1/134
1/134
3/134
0/134
5/134
1/134
1/134
4/134
0/134
1/134
0/134
21 63
48/133
II 1
I/ 1
e
e
e
e
e
e
e
e
e
undetected
e
e
e
e
undetected
e
undetected
e
HY-63-H1
HY-63-H1
a Detection frequency includes replicate analyses; maximum of 10 percent
replication. Original sample data listed in Appendix V.
b Locations are listed by area, station number, and horizon (i.e., CI-62-H2
is City Waterway, Station 62, second horizon).
c Indicates U.S. EPA priority pollutant number.
3.30
-------
TABLE 3.7. (Continued)
d Qualifiers:
B: Value corrected for "blank" contributions down to the detection
limit.
E: Estimated value.
N/R: Not reported.
U: Undetected at the detection limit stated (ug/kg or ppb dry weight
sediment).
Z: Value corrected for "blank" contributions; resulting value still
exceeds the detection limit.
e Compound detected at low concentration between minimum and maximum detection
limits at a few stations only.
f The high concentrations of tri- and tetrachloroethene prevented detection
of other volatile compounds at low levels in the single subsurface sample
analyzed. Blair Waterway volatiles data for Port of Tacoma Dredging Survey
samples are not reported, but volatiles were typically undetected at 5
ug/kg in these samples.
3.31
-------
TABLE 3.8. ORGANIC COMPOUNDS WITH AT LEAST A FIVEFOLD DIFFERENCE
BETWEEN MAXIMUM SUBSURFACE AND SURFACE SEDIMENT CONCENTRATIONS
Ratio of Maximum Observed Concentrations3
{Subsurface Concentration Exceeds
Surface Concentration)
2-methyl phenol 19
2,4-dimethylphenol 30
2,4,5-trichlorophenol 8.1
pentachlorophenol 16
2-methylnaphthalene 6.8
phenanthrene 7.1
anthracene 16
fluoranthene 16
pyrene 22
benzo(a)anthracene 13
chrysene 11
total benzofluoranthenes 7.5
benzo(a)pyrene 5.9
1,3-dichlorobenzene 6.7
1,4-dichlorobenzene 41
1,2-dichlorobenzene 5.4
hexachlorobenzene (HCB) 13
trichlorobutadiene isomers 2.1&
tetrachlorobutadiene isomers 28
pentachlorobutadiene isomers 36
hexachlorobutadiene 61
dimethyl phthalate 12
(Surface Concentrations Exceeds
Subsurface Concentration)
4-methylphenol 0.11
2,4,6-trichlorophenol 0.13C
di-n-butylphthalate 0.2
benzoic acid 0.1
aniline 0.03C
a Maximum subsurface concentration divided by the maximum surface
concentration.
b Included for comparison with other butadiene isomers.
c Undetected in subsurface sediment; detection limit used for calculation,
3.32
-------
3.1.4.3 Sediment Organic Compounds of Concern--
The range of organic compound concentrations in sediments from Puget
Sound reference areas is summarized in Table 3.9. These data are compiled
from this study (Carr Inlet) as well as from previous investigations funded
by various agencies throughout Puget Sound. Data for several compounds
were available only for the current study of Carr Inlet because full-scan
analyses were not always conducted in other areas. Detection limits in
some reference areas exceeded 50 ug/kg DW for several compounds. Detection
limits for recent Carr Inlet samples ranged from 0.5 to 50 ug/kg DW for
almost all compounds. To provide a comparable data set, a maximum detection
limit of 50 ug/kg DW was set for the acceptance of data from other reference
sites included in the ranges reported in Table 3.9.
Eighteen organic compounds and compound groups are of concern because
their concentrations (DW) in Commencement Bay surface sediments exceed
the concentration ranges for Puget Sound reference sediments. These organic
chemicals of concern are listed in Table 3.10. Compounds listed in Table 3.10
were detected at elevated levels at several stations within an area, and
often in several areas. Chemicals with similar distributional patterns
throughout Commencement Bay sediments, as demonstrated by statistical
correlations, and/or with closely related chemical behavior (e.g., chlorinated
benzenes) have been combined into contaminant groups for ease of analysis.
Results of statistical correlation analyses for inorganic and organic
contaminants over the entire study area and within large areas (i.e., Hylebos,
Blair, and City Waterways) are presented Section 3.1.5.
Of the six groups listed in Table 3.10, only the phthalates do not
always show a spatial correlation among individual phthalates within the
group. The chlorinated benzenes showed good correlation among individual
compounds (i.e., r=0.7 to r=0.98) with the exception of 1,3-dichlorobenzene
which was moderatley correlated (i.e., r=0.55 to r=0.63). This lack of
spatial correlation is most likely the result of different sources for
the chemicals rather than analytical variability. Individual components
of these groups will be discussed as appropriate w hen specific contaminated
areas are reviewed.
Organic compounds listed in Table 3.5 as undetected in all Commencement Bay
and Carr Inlet sediments are not considered to be of concern. Substances
found at only a few stations at low parts per billion levels (and often
below the detection limits of most other stations) are also not of general
concern. Six compounds not included in Table 3.10 were detected at levels
greater than the maximum observed in Puget Sound reference areas, but only
in one or two samples. These compounds include 2,4,6-trichlorophenol,
2,4,5-trichlorophenol, bis-2-chloroethoxymethane, 2,4-dinitrotoluene, aniline,
and 1,1,2-trichloroethane. While these compounds were not detected at
a sufficient number of sites to warrant statistical analysis of their spatial
distributions and potential relationships to sediment toxicity or biological
effects, sites contaminated with these compounds will be discussed. The
possible contribution of these compounds to observed toxicity or biological
effects at these selected sites will also be considered.
3.33
-------
TABLE 3.9. SUMMARY OF ORGANIC COMPOUND CONCENTRATIONS
IN SEDIMENTS FROM PUGET SOUND REFERENCE AREAS
Substance*
Range
(ug/kg dry
wt)
Mean
(ug/kg dry wt)
Detection
Frequency
Reference
Sitesb
Phenols
65
HSL
HSL
34
phenol
2-methyl phenol
4-methyl phenol
2, 4-d imethyl phenol
U
U
U
U
10 -
10
10 -
1 -
U
62C
32
10
lid
14
- 376
—
- 20
—
3/13
0/4
2/4
0/6
1,2
1
1
,3
Substituted Phenols
24
31
22
21
HSL
64
57
59
60
58
Low
55
77
1
80
81
78
HSL
High
39
84
72
76
74
75
73
83
82
79
2-chlorophenol
2,4-dichlorophenol
4-chloro-3-methyl phenol
2,4,6-trichlorophenol
2,4,5-trichlorophenol
pentachlorophenol
2-nitrophenol
2,4-dinitrophenol
4,6-dinitro-o-cresol
4-nitrophenol
Molecular Weight Aromatic
naphthalene
acenaphthylene
acenaphthene
f luorene
phenanthrene
anthracene
2-methyl naphthalene
Molecular Weight Aromatic
fluoranthene
pyrene
benzo(a)anthracene
chrysene
benzo( b) f 1 uoranthene
benzo(k) fluoranthene
benzo(a)pyrene
i ndeno(l, 2, 3-c,d) pyrene
dibenzo( a, h) anthracene
benzo(g,h ,i) perylene
U
U
U
U
U
U
U
U
0.5 -
0.5 -
0.5 -
0.5 -
10
0.1 -
0.1 -
0.5
0.5 -
0.5 -
U
U
U
U
U
U
U
U
5
10
10
10
50
10
100
100
0.02
___
—
—
—
• _~
- 33
—
—
—
—
0/6
0/6
0/6
0/6
0/4
1/6
1/6
0/6
0/6
0/6
1
1
1
1
1
1
1
1
1
1
Hydrocarbons
U
U
U
U
U
0.5 -
0.1 -
0.1 -
0.1 -
5 -
0.5 -
1 -
U
U
U
U
40
40
40
40
170
40
20
5.6
0.08
0.48
3.0
19
2.7
7.5
- 22
- 17
- 17
- 19
- 35
- 22
- 9.5
10/20
1/20
4/20
7/21
11/17
7/17
6/10
1,2,3,
1 ? }
1,2,3,
Al
1,2,3
1,2,3
1,4,
4,5,
4 S
4,5,
1
,6,7
,6,7
5,6
6
6
6
Hydrocarbons
U
U
U
U
U
7 -
8 -
4 -
5 -
5 -
5 -
0.37-
0.37-
0.4 -
3 -
U
U
U
100
120
40
40
94
94
40
30
5
20
32
30
3.7
6.4
17
17
9.3
7.4
0.08
3.8
- 41
- 41
- 23
- 26
- 33
- 33
- 10
- 9.2
- 4.1
- 7.2
17/22
16/22
8/17
8/17
12/21
12/21
10/14
6/12
1/5
2/6
Al
Al
1,2,3
1,2,3
Al
Al
1,3,4,
1,4,5
1
1,
1
1
,6,7
,6,7
1
1
5,6,
,6,7
7
7
3.34
-------
TABLE 3.9. (Continued)
Chlorinated Aromatic Hydrocarbons
26 1,3-dichlorobenzene
27 1,4-dichlorobenzene
25 1,2-dichlorobenzene
8 1,2,4-trichlorobenzene
20 2-chloronaphthalene
9 hexachlorobenzene (HCB)
Chlorinated Aliphatic Hydrocarbons
12 hexachloroethane
xx trichlorobutadiene
xx tetrachlorobutadiene isomers
xx pentachlorobutadiene isomers
52 hexachlorobutadiene
53 hexachlorocyclopentadiene
Halogenated Ethers
18 bis(2-chloroethyl) ether
42 bis(2-chloroisopropyl) ether
43 bis(2-chloroethoxy)methane
40 4-chlorophenyl phenyl ether
41 4-bromophenyl phenyl ether
Phthalate Esters
71 dimethyl phthalate
70 diethyl phthalate
68 di-n-butyl phthalate
67 butyl benzyl phthalate
66 bis(2-ethylhexyl)phthalate
69 di-n-octyl phthalate
Miscellaneous oxygenated compounds
54 isophorone
HSL benzyl alcohol
HSL benzoic acid
129 2,3,7,8-tetrachloro-
dibenzo-p-dioxin
HSL dibenzofuran
U 0.06- U 40
U 0.06- U 40
U 0.06- U 40
U 0.5- U 5
U 0.5- U 50
0.01- U 10
U 0.5- U 50
U 0.03- U 25
U 0.04- U 25
0.03- U 25
U 0.03- U 25
not analyzed
0.3 - U 10
U 0.5 - U 10
U 10
U 0.5 - U 5
U 0.5 - U 5
U 0.5 - U 50
9.0 - 11
U 20 - 760
U 0.5 - U 25
U 0.5 - U 25
U 0.5 - U 25
U 0.5 - U 130
U 10
U 25 - 430
not analyzed
U 5
Organonitrogen Compounds
HSL aniline U 1.0
56 nitrobenzene U 0.5
63 n-nitroso-di-n-propylamine U 0.5
HSL 4-chloroaniline U 50
HSL 2-nitroaniline U 50
20
5
10
0.004 - 19
0.004 - 19
0.004 - 19
0.07 - 3.5
4-18
160 - 170
210 - 216
1/18
1/18
1/18
0/6
0/6
6/12
1,2,3,4,5
1,2,3,4,5
1,2,3,4,5
1
1
1,4,5,6
...
0.27 -
1.6 -
0.15 -
0.07 -
7.9
9.2
7.7
8.5
0/6
5/12
5/12
5/12
5/12
1
1,4,5,6
1,4,5,6
1,4,5,6
1,4,5,6
1/6
0/6
0/6
0/6
0/6
0/5
4/5
3/5
0/5
0/5
0/5
0/5
0/4
3/4
0/4
0/6
0/5
0/5
0/4
0/4
3.35
-------
TABLE 3.9. (Continued)
HSL 3-nitroaniline U 50 — 0/4 1
HSL 4-nitroaniline U 50 — 0/4 1
36 2,6-dinitrotoluene U 0.5 - U 10 --- 0/5 1
35 2,4-dinitrotoluene U 0.5 - U 5 --- 0/5 1
62 n-nitrosodiphenylamine II 0.5 - U 5 — 0/5 1
37 1,2-diphenylhydrazine U 0.5 - U 5 --- 0/6 1
5 benzidine (4,4'-diamino-
biphenyl) U 0.5 --- 0/2 1
28 3,3'-dichlorobenzidine U 0.5 - U 100 — 0/6 1
Pesticides
93 p.p'-DDE U 10 - U 25 — 0/5 1
94 p.p'-DDD U 10 - U 25 — 0/6 1
92 p,p'-DDT U 10 - U 25 — 0/5 1
89 aldrin U 10 - U 25 — 0/6 1
90 dieldrin U 10 - U 25 — 0/6 1
91 chlordan U 10 - U 25 —- 0/6 1
95 alpha-endosulfan U 10 - U 25 --- 0/5 1
96 beta-endosulfan U 10 - U 25 — 0/5 1
97 endosulfan sulfate U 10 - U 25 — 0/5 1
98 endrin U 10 - U 25 --- 0/6 1
99 endrin aldehyde U 10 - U 25 — 0/5 1
100 heptachlor U 10 - U 25 — 0/6 1
101 heptachlor epoxide U 10 - U 25 — 0/6 1
102 alpha-HCH U 10 - U 25 —- 0/6 1
103 beta-HCH U 10 - U 25 — 0/6 1
104 delta-HCH U 10 - U 25 --- 0/6 1
105 gamma-HCH (lindane) U 10 - U 25 --- 0/6 1
113 toxaphene U 10 — 0/2 1
PCBs
xx Total PCBs (primarily
1254/1260) 3.1 - U 20 1.8 - 12 7/19 1,2,3,4,6,7
Volatile Compounds
85 tetrachloroethene
38 ethylbenzene
U 4.1 - U 16
U 4.1 - U 16
0/8
0/8
2,3
2,3
a Number indicates U.S. EPA priority pollutant number. HSL indicates Hazardous Substance List
compound.
b Reference sites: 1. Carr Inlet 4. Case Inlet 7. Nisqually Delta
2. Samish Bay 5. Port Madison
3. Dabob Bay 6. Port Susan
c An anomalously high phenol value of 1,800 ug/kg dry weight was found at one Carr Inlet station.
For the purposes of reference area comparisons, this value has been excluded.
d Mean calculated using 0.00 for undetected values.
e Mean calculated using the reported detection limit for undetected values.
References:
(Site 1) This report; Mowrer et al. (1977).
(Site 2) Battelle (1985).
(Site 3) Battelle (1985); Prahl and Carpenter (1979).
(Site 4) Mai ins et al. (1980); Mowrer et al. (1977).
(Site 5) Mai ins et al. (1980).
(Site 6) Mai ins et al. (1981).
(Site 7) Barrick and Prahl (in prep); Mowrer et al. (1977).
3.36
-------
TABLE 3.10. COMPARISON OF THE RANGE IN ELEVATIONS
ABOVE REFERENCE (EAR) FOR ORGANIC CONTAMINANTS OF CONCERN
IN SURFACE SEDIMENTS FROM COMMENCEMENT BAY
Elevation Above Reference*
Range
phenol
2-methyl phenol
4-methyl phenol
2, 4-dimethyl phenol
pentachlorophenol
LMW aromatic hydrocarbons6
HMW aromatic hydrocarbons^
chlorinated benzenesQ
chlorinated butadienes*1
total phthalatesi
total PCBsJ
2-methyl naphthal ene
benzyl alcohol
benzoic acid
dibenzofuran
n-nitrosodipheny lamine
tetrachloroethene
ethyl benzene
total xylenes
0.1
0.1
0.08
0.07
0.01
1.1
1.0
0.1
0.03
0.01
0.5
0.3
1.0
0.01
0.3
0.07
1.0
1.0
1.0
57
- 14
- 7200
- 31
- 26
- 570
- 450
- 64
- 1100
- 36
- 330
- 330
- 50
- 55
- 540
- 150
- 21
5
8
Median
3.4
0.38
8.3
1.5
1.5
36.
59.
3.4
2.8
1.9
11
44.
2.3
0.17
30.
1.2
1.0
1.0
1.0
Threshold'
1.7
l.Od
1.6d
1.5 Threshold^
HY.BL.SP,
MD.CI
SP.CI.RS
ATL SP
RS
J3L.MD
RS,CI,HY,MD,
~~ SI.SP
ALL HY
noneTTY
HY,BL
TIT
W.RS
ALL RS
HY.CI.SP
T3U
ATL RS
RS,BL,CI,HY,
~ SI
HY
none HY
none W
a Dry-weight concentration in Commencement Bay sediments divided by the
average concentration measured in six Carr Inlet reference sediments.
b The threshold EAR is defined as the ratio of the maximum reference sediment
concentration in Puget Sound divided by the average for six Carr Inlet
reference sediments. Above the threshold EAR, the dry-weight concentration
of a CorrnienceTient Bay sediment contaminant would exceed the maximum concentra-
tion (or detection limit) reported for any Puget Sound reference site listed
in Table 3.9.
3.37
-------
TABLE 3.10. (Continued)
c The contaminant EAR in sediment from at least one station in each area
listed exceeded the threshold level by an order of magnitude. Sediments
in underlined areas had the highest observed values. "ALL" indicates that
at least some sediment samples in all areas exceeded the threshold by an
order of magnitude. "None" indicates that no sediment values exceeded
lOx threshold; the area with the highest value is still listed.
d Compound has not been detected in any Puget Sound reference area to date.
The method detection limit has been used for a threshold value.
e Low molecular weight (LMW) aromatic hydrocarbons (1-3 rings) include
naphthalene, acenaphthylene, acenaphthene, fluorene, phenanthrene, and
anthracene.
f High molecular weight (HMW) aromatic hydrocarbons (4-6 rings) include
fluoranthene, pyrene, benzo(a)anthracene, chrysene, total benzofluoranthenes-
benzo(a)pyrene, indeno(l,2,3-c,d)pyrene, dibenzo(a,h)anthracene, and benzo-
(g,h,i)perylene.
9 Chlorinated benzenes include 1,3-dichlorobenzene, 1,4-dichlorobenzene,
1,2-dichlorobenzene, 1,2,4-trichlorobenzene, and hexachlorobenzene.
h Chlorinated butadienes include tri-, tetra-, and pentachlorobutadiene
isomers, and hexachlorobutadiene.
* Phthalates include dimethyl, diethyl, di-n-butyl, butylbenzyl, bis(2-
ethylhexyl), and di-n-octyl phthalates.
J Total PCBs is the sum of the detected Aroclors, typically Aroclor 1254
and 1260.
^ Reference data not available; value is based on the method detection
limit of 10 ug/kg (dry weight). These volatile compounds were undetected
at over 20 Commencement Bay sites.
3.38
-------
3.1.5 Priorltization of Areas Based on Sediment Contamination
To prioritize problem areas according to the steps outlined as part
of the Commencement Bay Decision-Making Approach (Tetra Tech 1984a), the
extent of sediment contamination was examined on three spatial scales:
areas (waterways and the Ruston-Pt. Defiance Shoreline), segments within
areas, and individual stations. Most inorganic and organic contaminants
of concern (Tables 3.4 and 3.10) were distributed heterogeneously in Commence-
ment Bay sediments. The following sections provide a description of how
study area segments were defined for use in data analysis and a discussion
of the results of spatial correlation analyses used to define groups of
chemicals having similar sources or fates. Changes in concentrations of
individual or groups of chemicals are then examined among study areas,
segments, and chemical "hotspots" within segments to prioritize sediments
by their level and spatial extent of contamination.
3.1.5.1 Definition of Study Area Segments--
Commencement Bay study areas were divided into twenty segments as
shown in Figure 3.6 and summarized in Table 3.11. The major reason for
defining segments was to provide a means of reporting major chemical, sediment
toxicity, and biological gradients within areas that sometimes contained
dozens of stations in various arrays. Hence, small areas such as Sitcum,
Milwaukee, St. Paul, and Middle Waterways were not further divided. Boundaries
of segments within large areas were generally established to define major
zones of varying chemical contamination. Contamination from one group
of chemicals sometimes extended well past a segment boundary defined according
to a zone of contamination for other chemicals.
At a minimum, each segment was required to contain at least three
stations (except segment CIS2 comprising the isolated Wheeler-Osgood branch
of City Waterway). Segments were also required to contain at least one
station for which complementary biolgical and sediment toxicity data were
available (except segment BLS4 located in deep water outside of Blair
Waterway). Average concentrations of chemicals within segments are used
in later discussion to evaluate trends in chemical concentrations along
areas. "Hotspots" of chemical contamination are evaluated at individual
stations when chemical gradients are apparent within segments.
3.1.5.2 Spatial Correlations Among Sediment Contaminants--
Linear correlation analyses were conducted to define groups of chemicals
having similar sources or depositional fates. All tests were based on
Spearman's correlation test (SPSS 1984). Covarying chemical groups were
defined as those showing a high degree of correlation in tests with the
entire data set (maximum of n=148, including replicate analyses), with
Hylebos Waterway data only (n=45), with Blair Waterway data only (n=38),
or with City Waterway data only (n=15). Subsets of the entire data set
were examined to ensure that apparent correlations were not artifacts of
extreme concentrations in a single area and to discriminate local distribution
patterns within the larger waterways. Scatterplots of the concentrations
of chemicals showing strong correlations, and those having unexpectedly
weak correlations, were examined for outliers. Correlations of metals
3.39
-------
COMMENCEMENT
BAY
HYS1
CIS3
CIS1
1 CITY l
WATERWAY
Area segments defined for Commencement Bay
Superfund data analysis.
-------
RSS3
u>
RUSTON
N
0 4000
' ' I » ' FEET
—1 METERS
T
1000
COMMENCEMENT
BAY
TACOMA
Figure 3.6. (Continued)
-------
TABLE 3.11. COMMENCEMENT BAY AREA SEGMENTS USED FOR DATA ANALYSIS
Segment
Relevant Sediment Stations
HYLEBOS WATERWAY:
HYS1 - Hylebos Upper Turning Basin
HYS2 - Hylebos Lower Turning Basin
HYS3 - Hylebos off Lincoln Ave
HYS4 - Hylebos above llth Street
HYS5 - Lower Hylebos Waterway
HYS6 - Outside Hylebos Waterway
BLAIR WATERWAY
BLS1 - Blair Upper Turning Basin
BLS2 - Blair Waterway Lincoln to llth
BLS3 - Lower Blair Waterway
BLS4 - Outside Blair Waterway
HY-11, HY-12, HY-13, HY-14, HY-
15, HY-16, HY-17, HY-18, HY-19
[9 stations including 3 biology]
HY-20, HY-21, HY-22, HY-23, HY-
24, HY-25, HY-26
[7 stations including 3 biology]
HY-01, HY-27, HY-28, HY-29, HY-
30, HY-31
[6 stations including 1 biology]
HY-32, HY-33, (HY-34), HY-35
[4 stations including 1 biology]
HY-02, HY-03, HY-36, HY-37, HY-
38, HY-39, HY-40, HY-41, HY-42,
HY-43, HY-44, HY-45, HY-46, HY-
47, HY-48
[15 stations including 5 biology]
HY-49, HY-50, HY-51, CB-11
[4 stations including 1 biology]
BL-01, BL-11, BL-12, BL-13, BL-
14, BL-15, B-02, B-ll, B-12
[9 stations including 3 biology]
BL-02, BL-16, BL-17, BL-18, BL-
19, BL-20, BL-21, BL-22, BL-23,
BL-24, BL-25, BL-26, B-03, B-04,
B-07, B-14, B-15
[17 stations including 5 biology]
BL-03, BL-04, BL-27, BL-28, BL-
29, BL-30, BL-31, BL-32, B-09,
B-10, B-17, B-18
[12 stations including 4 biology]
CB-12, CB-13, CB-14
[3 stations; NO biology stations]
3.42
-------
TABLE 3.11. (Continued)
SITCUM WATERWAY (SIS1):
MILWAUKEE WATERWAY (MIS1)
ST. PAUL WATERWAY (SPS1):
SI-11, SI-12, SI-13, SI-14, SI-
15
[5 stations Including 3 biology]
MI-01, MI-11, MI-12, MI-13, MI-
14, MI-15
[6 stations Including 3 biology]
SP-11, SP-12, SP-13, SP-14, SP-
15, SP-16
[6 stations Including 5 biology]
MIDDLE WATERWAY (MDS1):
MD-01, MD-11, MD-12, MD-13
[4 stations including 1 biology]
CITY WATERWAY:
CIS1 - City Waterway above llth St,
CIS2 - Wheeler-Osgood Waterway
CI-01, CI-03, CI-11, CI-12, CI-
13, CI-14, CI-15, CI-17, CI-18
[9 stations including 3 biology]
CI-02, CI-16
[2 stations including 1 biology]
CIS3 - City Waterway below llth St.
CI-19, CI-20, CI-21, CI-22
[4 stations including 2 biology]
RUSTON-PT. DEFIANCE SHORELINE:
RSS1 - Eastern Shoreline
RS-02, RS-04, RS-11, RS-12, RS-
13, RS-14, RS-15
[7 stations including 3 biology]
RSS2 - Shoreline at ASARCO outfalls
RS-03, RS-16, RS-17, RS-18, RS-
19, RS-20, RS-21
[7 stations including 3 biology]
RSS3 - Pt. Defiance
RS-22, RS-24
[2 stations including 2 bioassay only]
3.43
-------
and organic compounds were tested for concentrations normalized to dry
sediment weight, to total organic carbon (TOC), and to the total percent
of fine-grained material.
The strongest correlations for most substances were found when concen-
trations were normalized to TOC (especially organic compounds) or percent
fine-grained material (especially metals) (see Section 3.1.2). Correlation
coefficients for organic and inorganic chemicals having moderate to strong
intercorrelations (i.e., r >0.7 to 1.0) are summarized in Appendix II.
Inorganic chemicals of concern with at least moderate spatial correlations
(i.e., r >0.7) among chemical pairs in the total data set and in data subsets
for Hylebos and City Waterways were:
• Copper, lead, and zinc (r=0.85 to 0.98, n=143 total data
set; r=0.73 to 0.88, n=45 Hylebos Waterway; r=0.77 to 0.95,
n=15 City Waterway; all concentrations normalized to percent
fine-grained material).
Some strong correlations of metal concentrations in the entire data
set resulted simply from the inclusion of high concentration values for
most metals at stations off the ASARCO outfalls on the Ruston-Pt. Defiance
Shoreline. Copper, lead, and zinc were the only metals of concern whose
distributions appeared to be well-cor related within most study areas (i.e., even
when Ruston-Pt. Defiance values were excluded), although their correlation
among Blair Waterway samples was poor (i.e., r <0.4; n=38). These three
metals are treated in later sections as one group for ease of analysis.
Compositional variations among the metals in areas such as Blair Waterway
will be discussed as appropriate.
Major organic compound groups showing the best correlations among
compound pairs in the entire data set were:
• Chlorinated butadiene congeners (tri-, tetra-, penta-, and
hexachlorinated butadienes; r=0.97 to 1.0; TOC normalized
concentrations; n=136)
• Chlorinated benzenes (r=0.55 to 0.98; TOC normalized concen-
trations; n=144)
0 Low molecular weight aromatic hydrocarbons (r=0.50 to 0.94;
TOC normalized concentrations; n=144)
• High molecular weight aromatic hydrocarbons (r=0.59 to 0.94;
TOC normalized concentrations; n=144).
Correlations were often strengthened when data subsets were examined
(e.g., intercorrelations among low molecular weight aromatic hydrocarbons
in City Waterway ranged from r=0.83 to 0.98; n=15). Weaker correlations
over the entire study area are attributed to changing compositions of chemicals
emitted by different sources among study areas. Distributions of three
of the chlorinated benzenes (i.e., 1,2,4-trichlorobenzene, hexachlorobenzene,
and 1,4-dichlorobenzene) were well-correlated with the distribution of
3.44
-------
chlorinated butadienes (i.e., r >fl.89). There was also an overlap in the
distribution of low and high molecular weight aromatic hydrocarbons, especially
among 3- and 4-ring aromatic hydrocarbons.
Compounds with correlations at the lower end of the range reported
for compound groups were often present in low concentration (e.g., dibenzo(a,h)-
anthracene in the high molecular weight aromatic hydrocarbon group). Such
compounds are subject to greater analytical variability than other compounds
of the defined groups. Other compounds with lower correlations in these
groups apparently have additional sources not shared by the other components
(e.g. 1,3-dichlorobenzene in the chlorinated benzene group). In the latter
case, the defined groups are used in later sections only to indicate the
magnitude of contamination by the group; individual components of the group
are analyzed separately during source determinations in defined problem
areas.
Nonpriority pollutant hazardous substance list compounds and additional
tentatively identified compounds with concentration distributions that
tended to correlate with those of the chemical groups already defined include:
• Dibenzofuran, and tentatively identified compounds including
dibenzothiophene, 2-methylnaphthalene, methylphenanthrenes,
and biphenyl with aromatic hydrocarbons (especially 1- to 3-ring
compounds; r=0.66 to 0.89; TOC normalized concentrations;
n=121)
• Pentachlorocyclopentane (isomer; tentative identification)
with 1,2,4-trichlorobenzene, hexachlorobenzene, 1,4-dichloro-
benzene, and chlorinated butadienes (r=0.89 to 0.98; TOC
normalized concentrations; n=123).
Concentrations of some chemicals showed strong correlations only within
a single area (e.g., Hylebos Waterway). Those combinations of inorganic
and organic chemicals with strictly local importance are discussed when
individual problem areas are reviewed in Section 6.
3.1.5.3 Relative Magnitude of Contamination Among Study Areas--
Concentrations of the chemicals of concern listed in Tables 3.4 and 3.10
(i.e., those found at concentrations that exceed Puget Sound reference
conditions) varied in some cases over five orders of magnitude in Commencement
Bay surface sediments. Concentrations (DW) of the four inorganic and six
organic contaminants listed in Table 3.12 exceeded 1,000 times reference
conditions at individual Commencement Bay stations. Concentrations of
metals were elevated to this degree only in sediments at three stations
directly off the three major ASARCO outfalls on the Ruston-Pt. Defiance
Shoreline. Concentrations of arsenic and antimony averaged over all stations
in segment RSS2 (Figure 3.6) along the Ruston-Pt. Defiance Shoreline were
also elevated over 1,000 times reference conditions.
Organic compound concentrations exceeded 1,000 times reference conditions
only in sediments from selected stations in Upper and Lower Hylebos Waterway,
from stations directly off the main Champion International outfall in St. Paul
Waterway, and from a single station directly off the main ASARCO outfall
3.45
-------
TABLE 3.12. SUMMARY OF CHEMICALS WITH ELEVATIONS ABOVE REFERENCE (EAR)
GREATER THAN l.OOOX IN SEDIMENTS FROM COMMENCEMENT BAY
Chemicals Exceeding l,000x Reference
Station
ORGANIC COMPOUNDS:
benzo(a)pyrene
4-methyl phenol
2-methyoxyphenol
phenanthrene
trichlorobutadienes
tetrachlorobutadienes
HY-22
SP-14
SP-14,-15
RS-18
HY-43,-46,-47
HY-46
METALS:
antimony
arsenic
copper
mercury
RS-17,-18,-21
RS-17,-18,-21
RS-17,-18,-21
RS-18
Chemicals Exceeding l.OOOx Reference9
Area or Segment
ORGANIC COMPOUNDS:
4-methylphenol
2-methoxyphenol
St. Paul Waterway
St. Paul Waterway
METALS:
antimony
arsenic
RSS2
RSS2
a Concentration averaged over all stations in the area or segments indicated,
3.46
-------
on the Ruston-Pt. Defiance Shoreline. Concentrations of two phenolic compounds
averaged over all stations in St. Paul Waterway exceeded 1,000 times reference
conditions.
Twenty-eight chemicals or chemical groups with sediment concentrations
(DW) at one or more stations that were elevated between 100 and 1,000 times
reference conditions at Carr Inlet are listed in Table 3.13. Station locations
are also indicated. All metals of concern except nickel were found at
these levels, primarily at stations along the Ruston-Pt. Defiance Shoreline.
Similar elevations in concentrations of organic compounds were more widespread
throughout the Commencement Bay study area (Table 3.13).
Sediment concentrations between 100 and 1,000 times Carr Inlet reference
conditions were also observed for 17 of these 28 substances after averaging
over multiple stations in an area or segment (Table 3.14). For metals,
such high average elevations were found only along the Ruston-Pt. Defiance
Shoreline, and in segments RSS2 and RSS3 of the shoreline. For organic
compounds, such high average elevations were found in all study areas except
Blair Waterway and the Ruston-Pt. Defiance Shoreline (Table 3.14). The
potential relationships among these contaminants and observed sediment
toxicity and biological effects are discussed in Section 4.
Distributions of eight major chemicals or chemical groups of concern
among Commencement Bay study areas are shown in Figures 3.7-3.14. The
distributions of these chemicals give a perspective of the major zones
of contamination in Commencement Bay based on data collected under this
investigation. Distributions of the remaining chemicals of concern are
addressed in discussions of problem areas (Section 6). Each figure has
two key features. First, a pair of graphs is presented for each contaminant
or contaminant group. The upper graph of each pair shows the average magnitude
of contamination expressed as the elevation above reference (EAR) concentrations
measured at Carr Inlet. For example, a concentration of 100 ug/kg in the
study area relative to a concentration of 20 ug/kg in Carr Inlet would
result in an EAR of 5. The same data are presented in the lower graph
of each pair, but each average EAR has been recalculated as a percentage
of the largest average EAR observed among Commencement Bay areas. This
later data format is useful in visually demonstrating the relative contamination
among areas.
Second, to enable a comparison of the relative magnitude of contaminant
concentrations in sediments containing differing amounts of fine-grained
material and organic carbon, EAR reported in the figures are based on ratios
of sediment concentrations normalized three different ways. The first
bar shown for each area represents the magnitude of EAR calculated using
study area and reference area concentrations normalized to total dry weight
of sediment. EAR represented by the second bar are based on a ratio of
concentrations normalized to the weight of the fine-grained fraction only.
The third bar represents the EAR based on concentrations normalized to
the weight of the total organic carbon in each sample.
For example, in Figure 3.7 the sum of copper, lead, and zinc dry-weight
concentrations averaged over all sediments collected from the Ruston-Pt.
Defiance Shoreline is 120 times higher (i.e., EAR=120) than the sum of
the average dry-weight concentrations of these three metals in sediments
3.47
-------
TABLE 3.13. SUMMARY OF CHEMICALS WITH ELEVATIONS ABOVE REFERENCE (EAR)
BETWEEN 100 AND l.OOOX IN SEDIMENTS FROM COMMENCEMENT BAY STATIONS
Chemicals >100x and <1.000x Reference
Station
ORGANIC COMPOUNDS:
aromatic hydrocarbons
(4-6 rings; non-alky! ated)
aromatic hydrocarbons
(1-3 rings; non-alkylated)
l,l'-bipheny!
bis(2-ethy!hexyl)phthalate
coprostanol
dibenzofuran
dibenzothiophene
1,2-dichlorobenzene
isopimaradiene
kaur-16-ene [tentative id]
1-methyl-2-(1-methylethyl benzene)
2-methylnaphthalene
4-methylphenol
2-methylphenanthrene
BL-14; B-04; CI-01,02,03,11,12,
CI-13,15,17,21,22; HY-12 through
26,33,36; MD-11,12 ; MI -1 1 ;
RS-13,14,18,21; SI-11
CI-01,02,11,12,15,17,21,22 HY-16,22,23;
MD-11,12; RS-13,16,18,21; SI-14;
SP-13,14
RS-18
CI-12,13,15; HY-22
BL-04; CI-03,12; HY-03,41; MI-01;
SI-14; SP-11
CI-11,15; HY-22; MD-11,12; RS-13,16,
RS-18,21; SI-14; SP-13
RS-18
CI-16
BL-01,04,13,32; CI-03,12,17,20;
HY-15,16,36,42,43,47; MD-12;
MI-13,15; RS-04; SI-11,12; SP-11,12,14,15
BL-04; CI-03,11,20; HY-01,03,12,14,15,16,
17,22,25,28,29,31,33,35,37,40,41,42,43,47
MD-01,12; MI-11,15; RS-04; SI-11,12,15;
SP-11,12,14,15,16
SP-14; RS-16; SI-11
BL-16; CI-02,03,11,12,15,16,17,18,21,22;
HY-22,26,36,39; MD-11,12; MI-12;
RS-13,16,18,21; SI-14,15; SP-13,14
SP-13,14
BL-01,04,24,32; CI-03,12,15,17 through 22
HY-14,15,16,17,22,30,31,34,36,43,45;
MD-11,12,13; MI-11,13; RS-11,13,16,17,
RS-19,21; SI-11,12,14,15; SP-11,12
3.48
-------
TABLE 3.13. (Continued)
2-methylphenanthrene
1-methylphenanthrene
1-methylpyrene
2-methylpyrene
n-nitrosodiphenylamine
Total chlorinated butadienes
Total PCBs
RS-18; SP-14
RS-18
HY-16,17,22; RS-18
CI-20; HY-15,16,21,36; RS-18
RS-18
HY-22,25,28,33,36,37, HY-39 through
43,45,47,48
HY-03,22,23,27,42
METALS:
antimony
arsenic
cadmium
copper
lead
mercury
zinc
HY-16; RS-19,24
RS-19,24
RS-17,18,21
RS-19
RS-17,18,19,21
RS-17,21
RS-17,18,21
3.49
-------
TABLE 3.14. SUMMARY OF CHEMICALS WITH SEDIMENT
ELEVATIONS ABOVE REFERENCE (EAR) BETWEEN 100 AND l.OOOX
AVERAGED OVER COMMENCEMENT BAY AREAS OR SEGMENTS
Chemicals >100x and
-------
TABLE 3.14. (Continued)
total PCBs
METALS:
antimony
arsenic
copper
lead
mercury
HYS2
Ruston-Pt. Defiance
and RSS3
Ruston-Pt. Defiance
and RSS3
Ruston-Pt. Defiance
and RSS2
Ruston-Pt. Defiance
and RSS2
Ruston-Pt. Defiance
and RSS2
3.51
-------
120 -
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Figure 3.7. Elevations above reference (EAR) for Pb, Cu,
Zn in Commencement Bay study areas.
3.52
-------
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Figure 3.8.
Elevati
ons
above
reference (EAR) for arsenic
in Commencement Bay study areas.
3.53
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3.9
Elevations above reference
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ment Bay study areas.
3.54
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molecular weight aromatic hydrocarbons in
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3.55
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Figure 3.11. Elevations above reference (EAR) for total
PCBs in Commencement Bay study areas.
3.56
-------
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Figure 3.12. Elevations above reference (EAR) for total
chlorinated benzenes in Commencement Bay study
areas.
3.57
-------
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Figure 3.13. Elevations above reference (EAR) for total
chlorinated butadienes
in
Commencement Bay
study areas.
3.58
-------
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Figure 3.14.
Elevations above reference (EAR) for total
phthalates in Commencement Bay
study areas.
3.59
-------
from Carr Inlet. When normalized to the total percent fine-grained material,
the sum of average concentrations for copper, lead, and zinc in Ruston-
Pt. Defiance Shoreline sediments is approximately 70 times higher than
the average calculated for Carr Inlet sediments (i.e., EAR=70). The correspond-
ing EAR on an organic carbon basis is 19. In general, the greatest variations
among waterways were found for concentrations normalized to dry weight,
and the smallest variations were found for concentrations normalized to
organic carbon.
Data presented in Figures 3.7 and 3.8 show that the average metals
contamination along the Ruston-Pt. Defiance Shoreline is 5-50 times higher
than that in any other area, regardless of the method of normalization.
This extreme elevation in one study area only is not seen for low and high
molecular weight aromatic hydrocarbons (Figures 3.9 and 3.10). Among waterways,
comparatively low average elevations (e.g., less than 20 percent of the
maximum EAR regardless of the normalization) of high molecular weight aromatic
hydrocarbons were found only in St. Paul Waterway (Figure 3.10).
Normalized to sediment dry weight, average elevations of all of the
chlorinated organic compound groups (i.e., PCBs, chlorinated benzenes,
and chlorinated butadienes) were highest in Hylebos Waterway (Figures 3.11,
3.12, and 3.13). Average PCB concentrations (DW) in St. Paul and City
Waterways, and along the Ruston-Pt. Defiance Shoreline were also elevated
an order of magnitude over reference conditions (Figure 3.11). Dry-weight
elevations of chlorinated benzene concentrations did not exceed an order
of magnitude, but the average in several areas approached the average observed
in Hylebos Waterway (Figure 3.12). Total chlorinated butadienes were elevated
greater than an order of magnitude above reference conditions only in Hylebos
Waterway sediments, regardless of the concentration normalization used
(Figure 3.13).
Average elevations of total phthalate esters (Figure 3.14) did not
exceed 10 times reference conditions in any study area. Average concentrations
of phthalate esters in the Sitcum, Milwaukee, and St. Paul Waterways were
less than reference conditions, regardless of the concentration normalization
used.
Distributions of the same chemicals and chemical groups shown in Figures
3.7-3.14, but summarized on the basis of the average EARs observed in each
of the 20 segments (Table 3.11) are presented in Figures 3.15-3.22. The
format of each pair of graphs and the use of three different concentration
normalizations are identical to those just described for Figures 3.7-3.14.
Data for segments within each area are arranged from the mouth of each
waterway (left) to the head (right), and from the eastern end of the Ruston-
Pt. Defiance Shoreline (left) to the western end (right).
The high average EARs observed for metals along the Ruston-Pt. Defiance
Shoreline were limited to segment RSS2 and, to a lesser extent, RSS3 (Figures
3.15 and 3.16). Average EARs of these metals on a dry-weight basis in
the waterways tended to increase from the mouth to the head of larger waterways
(e.g., Hylebos, Blair, and City). EARs normalized to percent fine-grained
material tended to be more constant along the waterways.
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Figure 3.15. Elevations above reference (EAR) for Pb, Cu,
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3.61
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Figure 3.16.
Elevations above reference (EAR) for arsenic
by segment in Commencement Bay study areas.
3.62
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Figure 3.17.Elevations above reference (EAR) for low
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segment in Commencement Bay study areas.
3.63
-------
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Figure 3.18. Elevations above reference (EAR) for high
molecular weight aromatic hydrocarbons by
segment in Commencement Bay study areas.
3.64
-------
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Figure 3.20. Elevations above reference (EAR) for total
chlorinated benzenes by segment in Commence-
ment Bay study areas.
3.66
-------
CO
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Figure 3.21. Elevations above reference (EAR) for total
chlorinated butadienes by segment in Commence-
ment Bay study areas.
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Figure 3.22. Elevations above reference (EAR) for total
phthalates by segment in Commencement Bay
study areas.
3.68
-------
A similar tendency [i.e., higher EARs (DW) away from the mouths of
the waterways] was observed for aromatic hydrocarbons (Figures 3.17 and
3.18). An upwaterway gradient was most distinct for high molecular weight
aromatic hydrocarbon EARs normalized to dry weight in Hylebos Waterway
(Figure 3.18). Although Hylebos Waterway sediments contained the highest
observed levels of chlorinated organic compounds, the spatial distributions
of PCBs, chlorinated benzenes, and chlorinated butadienes were different
from each other within Hylebos Waterway (Figures 3.19-3.21). Highest average
PCB concentrations (DW) were found toward the head of Hylebos Waterway,
but total chlorinated butadiene and benzene concentrations were substantially
more elevated toward the mouth of Hylebos Waterway.
The distribution of phthalates in study area segments is shown in
Figure 3.22. High levels (DW) of phthalates were observed in sediment
samples from the head of City Waterway and from Wheeler-Osgood Waterway
in organic-rich sediments that were contaminated with other chemicals.
Unlike any of the other contaminant groups, the highest sediment elevations
of phthalates (DW) was found in segment HYS6 outside of Hylebos Waterway.
Sediment samples from segment BLS4, outside of Blair Waterway, had the
highest phthalate elevations in Blair Waterway. This similarity between
the two waterways, and the relatively low contamination levels in the outermost
segments by other chemical groups commonly associated with urban contamination,
suggests that phthalates have an independent source in this area. A potential
contribution from natural sources cannot be ruled out. The low phthalate
elevations in Sitcum, Milwuakee, and St. Paul Waterways adjacent to the
Puyallup River tend to suggest that discharges from the Puyallup River
are not the source.
The relative magnitude of concentrations of other chemicals showing
distributions similar to those summarized in Figures 3.17-3.22 are not
shown. Chemical characteristics of individual sites will be summarized
in detail in later discussions of problem areas (see Section 6).
3.1.6 Comparison with Historical Conditions
Concentrations of most chemicals measured in the current investigation
of Commencement Bay subtidal sediments are comparable to or higher than
surface sediment values measured in recent studies conducted by WDOE, U.S. EPA,
NOAA, and other groups. Available historical concentrations of metals
and organic compounds in subtidal and intertidal sediments from Middle
and Milwaukee Waterways, and from along the Ruston-Pt. Defiance Shoreline
are comparable to or lower than those in the present study. High levels
of chlorinated butadienes were observed at a single historical station
near Old Tacoma on the Ruston-Pt Defiance Shoreline, but repeated sampling
did not confirm the report. Few historical data were found for any sediment
contaminants along the Ruston-Pt. Defiance Shoreline or for organic compounds
within Middle Waterway. Concentrations of chemicals found during the
Commencement Bay Deep Water Sediment Investigation (Hileman and Matta 1983)
were lower overall than those found in the waterways during the present
investigation. Major differences between historical and current results
for metals and organic compounds in the remaining study areas are summarized
below. Phthalate ester concentrations are not compared because most historical
data were not corrected for potential laboratory contamination.
3.69
-------
3.1.6.1 City Waterway--
A single station with high PCB values (300-600 ug/kg DW) was measured
during 1980 NOAA studies west of the llth Street Bridge in City Waterway
(Mai ins et al. 1980). Much lower PCB values were observed in sediments
from this area in the present study (e.g., 20-100 ug/kg DW at Stations
CI-18, CI-19, and CI-20). A U.S. EPA 1981 study detected hexachlorobutadiene
(HCBD) (340 ug/kg dry weight) at the mouth of City Waterway (U.S. EPA 1982);
HCBO was undetected at a detection limit of 25 ug/kg DW in the present
study.
3.1.6.2 St. Paul Waterway--
Historical metals levels in sediments from St. Paul Waterway were
somewhat higher overall than the current findings, but were within a factor
of 10. PCBs had been detected in the middle of the waterway at 250 ug/kg
DW; the highest value in the current study was 79 ug/kg DW near the mouth
of the waterway. PCBs were undetected in sediments from remaining stations
at a detection limit of approximately 100 ug/kg DW. A single historical
pentachlorophenol value of 840 ug/kg DW was not confirmed in recent samples;
pentachlorophenol was undetected throughout the waterway at a detection
limit of 25-100 ug/kg DW.
3.1.6.3 Sitcum Waterway--
Copper, lead, and zinc data collected by Tetra Tech indicate an increasing
gradient in the concentrations of these metals toward the head of the waterway.
Historical data indicate a more patchy distribution with elevated concentrations
along the north shore and in the northeast corner (U.S. EPA/DOE 1981 station).
There is no consistent trend in concentration of those metals when all
data are considered. Concentrations of several aromatic hydrocarbons in
a single historical sediment sample collected during a 1981 U.S. EPA/DOE
study near Station SI-14 were more than 10 times currently observed concen-
trations. The unusually high proportion of benzo(a)pyrene relative to
other aromatic hydrocarbons in this historical sample was not found in
the current samples from Sitcum Waterway.
3.1.6.4 Blair Waterway--
Historical intertidal concentrations of PCBs at the north Lincoln
Avenue drain (740 ug/kg DW) were approximately 20 times higher than any
present concentrations in Blair Waterway subtidal samples from the same
area. Arsenic, chromium, copper, lead, and zinc concentrations at two
historical intertidal stations near the south Lincoln Avenue drain exceeded
10 times currently measured subtidal values in the same area. Station BL-14
toward the head of Blair Waterway near the north shoreline had higher
concentrations of organic compounds (primarily hydrocarbons) than any historical
Blair Waterway sample.
3.1.6.5 Hylebos Waterway--
The most extensive historical data set for sediment contaminants was
collected in Hylebos Waterway. At the head of the waterway (segment HYS1),
historical contaminant concentrations were comparable to or less than those
3.70
-------
measured in the current studies, with the exceptions of a single intertidal
sample near the Kaiser Ditch with high PCBs (980 ug/kg OW) and intertidal
samples with higher aromatic hydrocarbon concentrations,
In the lower turning basin near Stations HY-20 to HY-26 (segment HYS2),
historical intertidal sediment concentrations of chloroform, arsenic, copper,
and mercury exceeded currently measured subtidal sediment values, but by
less than a factor of 10, with the exceptions of chloroform (a factor of
220 over the detection limit of the current studies) and mercury (a factor
of 30). All historical intertidal samples were collected from the south
shore of the waterway. Historical subtidal sediment concentrations of
metals were comparable to those in the current study. The maximum historical
concentration of PCBs in surface sediments within this area was 1150 ug/kg
DW, approximately half the 2,000 ug/kg DW measured at Station HY-22.
Historical sediment concentrations of metals and organic compounds
in segment HYS3 near the Lincoln Avenue drain were in general agreement
with those from the current study. Subtidal sediments from Station HY-27
in this segment contained relatively high concentrations of PCBs (860 ug/kg
DW). Similarly high concentrations were observed at a nearby historical
subtidal station (>1,000 ug/kg DW), but an historical intertidal sample
collected near the Lincoln Avenue drain had much lower concentrations (170 ug/kg
DW). These data suggest that the drain may not be an ongoing source of
PCBs to the subtidal sediments, but that older sediments contaminated with
PCBs may have been exposed in the middle of the waterway.
PCB concentrations 10 times higher than those measured in the current
study were found in historical samples collected in segment HYS4 near Station
HY-32. Aldrin and alpha-HCH were also reported in historical samples,
but at concentrations near the detection limits attained in the current
study.
Concentrations of lead 35 times greater than those measured in the
current study were found in historical intertidal sediments on the south
side of Hylebos Waterway near Station HY-42 (segment HYS5). Historical
subtidal metal concentrations were comparable to those in the current study.
Higher hexachlorobutadiene, hexachlorobenzene, and PCB concentrations (3,300,
1,300, and 1,700 ug/kg DW, respectively) were reported historically in
surface sediments (0-2 cm) of this segment than in the current study.
However, HCBD and HCB concentrations in the surface interval of cores (e.g.,
0-15 cm) collected during the current study in this area were comparable
or higher than those in historical surface samples. Aldrin was also detected
at 62-950 ug/kg DW in historical intertidal and subtidal sediments collected
near HY-42, although the pesticide was undetected in the current study
at a detection limit of 50 ug/kg DW. As previously discussed, the historical
reporting of aldrin may be a false EC/6C identification of an interfering
chlorinated substance. There were no available historical data within
segment HYS6, which is outside of Hylebos Waterway.
With the exception of unconfirmed reports of selected pesticides (see
discussion in Section 3.1.4.1) in sediments from isolated stations, there
were no organic compounds or metals detected in historical Commencement
Bay studies that were not also found in the current studies. Besides the
differences summarized in this section, the major difference between the
3.71
-------
available historical studies and the current study is that a wider range
of chemicals were quantitated at typically lower detection limits in the
current study.
^3.1.7 Contamination of Waterway Suspended Solids
The water quality study was designed to provide a qualitative check
on the movement of contaminated particulate material among Commencement
Bay waterways. A survey of nine stations (two depth intervals) was conducted
in April, 1984 during a flood tide and high flow from the Puyallup River.
In August, 1984, sampling was conducted at the same locatons at ebb tide
and low flow from the Puyallup River. Stations were located in the Puyallup
River and Hylebos, Blair, Sitcum, Milwaukee, and City Waterways (see Figure
2.4). Water sampling in the upper portions of Hylebos, Blair, and City
Waterways was conducted to characterize the contaminant distribution within
these larger waterways.
For both April and August studies, the Puyallup River samples had
the highest total suspended solids (TSS) concentrations of all samples
collected (6.7 mg/L, 9.8 mg/L). The mouth of City Waterway had the lowest
surface TSS load (1.2 mg/L). Little difference was seen between April
and August TSS concentrations (except for the Puyallup River samples).
Vertical stratification between the surface and 5-m depth, as measured
by TSS ratios, also remained fairly constant between April and August.
The April data showed the presence of both HPAH and LPAH (200-8,900 ug/kg
DW) and phthalates (380-36,000 ug/kg DW) in all the sampled waterways.
Other organic compounds detected included: 4-methylphenol in the Puyallup
River (6,100 ug/kg DW), benzoic acid at the head of Blair Waterway (270,000
ug/kg DW) and dibenzofuran at the head of City Waterway (810 ug/kg DW).
No other organic compounds were detected above the relatively high analytical
detection limits obtained for this survey (500-50,000 ug/kg DW). Concentration
gradients of organic contaminants along the waterways were not observed
for the April study.
Most metals were detected in the particulate samples. Arsenic was
found in highest concentration (290 and 390 mg/kg DW for the subsurface
and surface samples, respectively) at the head of Hylebos Waterway. Arsenic
concentrations increased from the mouth to the head of Hylebos Waterway.
A similar gradient was observed in arsenic sediment concentrations in Hylebos
Waterway. However, the August particulate sample data showed no gradient
in arsenic concentrations, and the concentrations at the head of Hylebos
Waterway were much lower than previously observed (6.2 and 100 mg/kg DW
for the subsurface and surface samples, respectively). Concentrations
of arsenic in particulate material within Hylebos Waterway appear to be
related to existing Hylebos sources that fluctuate with time rather than
to a source from outside of the waterway. This conclusion is consistent
with the findings of a recent report on the log sort yards in the area
(Norton and Johnson 1985a).
Organic compound data from the August sampling effort provided more
information because of an approximately fivefold to tenfold increase in
analytical sensitivity compared with the April study. HPAH and LPAH were
the main organic compounds detected at the mouths of all the waterways
3.72
-------
sampled (43-6,600 ug/kg DW) . Additional compounds detected included:
4-methylphenol at the mouths of Sitcum Waterway, Milwaukee Waterway, and
the Puyallup River (2,900-6,600 ug/kg DW); pentachlorophenol at the head
of Blair Waterway (440 ug/kg DW); phthalates in all waterway samples except
those from Milwaukee Waterway (130-1,600 ug/kg DW); isophorone in Sitcum
Waterway (170-610 ug/kg DW); and dibenzofuran in Sitcum, Milwaukee, and
City Waterways, and the Puyallup River (65-330 ug/kg DW). No other compounds
were reported in any sample above the approximate 250-5,000 ug/kg DW detection
limits attained for these particulate samples.
There were no apparent horizontal concentration gradients in Blair
or City Waterways for any chemical detected during the the August sampling
period. Concentrations of HPAH increased slightly towards the head of
Hylebos Waterway (e.g., fluoranthene 610-4600 ug/kg DW). A similar gradient
of HPAH concentrations was observed in Hylebos Waterway sediments. As
discussed previously for arsenic, the observed distribution of HPAH on
Hylebos Waterway particulate material appears to reflect contributions
from intermittent local sources within Hylebos Waterway. These data do
not suggest that highly contaminated suspended particles are moving out
of Hylebos Waterway. In general, the chemical data for suspended solids
show little evidence of a major transport of contaminated particles into
or out of any of the the waterways sampled.
For both the April and August samples, the concentrations (DW) of
organic chemicals bound to suspended solids were more than 10 times higher
than the corresponding sediment concentrations. The concentrations of
metals bound to suspended solids were similar to those measured in waterway
sediment samples. The reasons for this relative difference in concentrations
for organic compounds and metals have not been determined. No major qualitative
differences in the composition of related substances (e.g., individual
PAH compounds) were found between the contaminants on suspended solids
and those in the underlying sediments.
3.1.8 Summary
A patchy distribution of contamination was observed in Commencement Bay.
Several contaminants were found at concentrations in excess of 1,000 times
reference conditions at a few locations. As a means of summarizing this
variable distribution, chemicals or chemical groups of concern for which
concentrations exceeded 80 percent of the values observed in all Commencement
Bay sediments analyzed are listed (by station) in Table 3.15. Where the
80th percentile value did not exceed the range observed for Puget Sound
reference areas, a higher percentile was used. The station listing is
organized by area and segment to show contiguous stations with high levels
of contamination.
The decision-making approach specifies that stations with chemical
concentrations exceeding the 80th percentile cutoff described be prioritized
for evaluation of potential source control. This chemical prioritization
of problem areas will be incorporated with later evaluations of the relation-
ships among sediment contamination, toxicity, and biological effects to
determine the final prioritization of problem areas for remedial action.
3.73
-------
TABLE 3.15. STATION LOCATIONS AT WHICH SEDIMENT CONCENTRATIONS OF
CHEMICALS EXCEEDED 80 PERCENT OF SEDIMENT CONCENTRATIONS
MEASURED IN ALL COMMENCEMENT BAY STUDY AREAS
Segment Station
Hrsi HY-11 |gc
HY-12 b Hg HPA
HY-13 As Hg HPA
HY-14 b HPA
HY-1S HPA
HY-16 CPZ As LPAH HPA
HY-17 b CPZ |As) HPA
HY-18 b CPZ As Hg HPA
HY-19 b CPZ As HPA
HYS2 HY-20 As HPA
HY-21 As HPA
HY-22 b CPZ (As) Hg LPAH HPA
HY-23 b As Hg LPAH HPA
HY-24 b CPZ As Hg HPA
HY-25 LPAH
HY-26 IHPA
HYS3 HY-01 CPZ [As]
HY-27
HY-28 b
HY-29
HY-3U
HY-31
HYS4 HY-32 b Hg
HY-33 HPA
HY-34
HY-35
HYS5 HY-36 Hg
HY-37 b
HY-38
HY-39
HY-02
HY-40 |Hg]
HY-41
HY-42 b
HY-43 b
HY-44 b
HY-45
HY-03
HY-46 Hg
HY-47 b
HY-48
HYSb HY-49
HY-50 b
HY-51
CB-11
BLS1 BL-11 b As
B-ll
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TABLE 3.15. (Continued)
Segment Station
SPS1 SP-11 b
SP-12 b
SP-13
SP-14 b
SP-lb b
SP-16 b
LPAH
LPAH
MOSI MD-ii ILPAH] HPAH
MD-Ol
MD-12 b CPZ LPAH
MD-13 [CPU As (Hg] LPAH
CISl CI-11 b
CI-12
CI-13 b
CI-14
CI-01
CI-lb
CI-17 b
CI-18
CI-03
CIS2 CI-02
CI-16 b
CIS3 Cl-19
Cl-20 b
Cl-21
CI-22 b
RSS1 RS-11
RS-12 b
RS-04
RS-13 b
RS-OZ
RS-14 b
RS-lb
RSS2 RS-16
RS-17
RS-20 b
RS-03
RS-19 b
RS-18 b
RS-21
RSS3 RS-24 b
RS-22 b
CPZ
CPZ
IP/
CPZ
CPZ
CPZ
CPZ
CPZ
[Hg] LPAH HPAH
LPAH
pg] LPAH IHPAHl
ICMil HPAH
LPAH
[Hg]
[HgJ LPAH
CPZ] Hg LPAH [HPAH] PCB
CPZ LPAH
LPAH IHPAHl
LPAH HPAH
Hg LPAH HPAH
CPZ
CPZ]
CPZ
CPZ
CPZ
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AS (Hgl ILPAH! PCB
As Hg PCB
AS [Hq]
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Chemical3
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MNOL BZAC IDBFI |BZOH| M
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MNOL DTP M
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CBEN [PNOT] | HNULl |PCP| [DBF] PHTH
PNOL IMNOL! [DBF] |PHTH| IAPAH! [DTP]
MNOL
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IMNOLI BZAC DBF BZOH PHTH] |APAH|
BZAC PHTH!
EB RET MOX |COP|
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OIB MOX
MNOL BZOH PHTH MOX
CBEN [DBF| BZOH |PHTH| DIB
PNOL MNOL DBF APAH DTP RET DIB MOX
[APAH] [DTP] MEB RET [c5p]
CBEN IPNOLI MNOL [DBFJ NOPA MEB
CBEN MNOL DBF |PHTH] iNOPAl DIB
BZAC
IPNOL! FATAH) IjjTgl M
MNOL DBF APAH
APAH
MNOL APAH
1 HNOL| |DBF| APAH
MNOL
PNOL | MNOLl |DBF| [PHTH] [M!
PHTH
CBEN PNOL DBF [ NOPA I [APAHl ME
DBF PHTH APAH
NDPA
IB I RET) IDIBI MOX
MOX
RET
|RET|
COP
RET
iBifirn OIB
B RET DIB
RET DIB
-------
TABLE 3.15 (Continued)
a Abbreviations used for chemicals are listed below:
PRIORITY POLLUTANTS AND ADDITIONAL HAZARDOUS SUBSTANCE LIST COMPOUNDS (analyzed
for at 138 stations except as noted)
CPZ = Copper, lead, zinc
AS = Arsenic
HG = Mercury
LPAH = Low molecular weight aromatic hydrocarbons
HPAH = High molecular weight aromatic hydrocarbons
PCB = Total PCBs
CBD = Total chlorinated butadienes
CBEN = Total chlorinated benzenes
PNOL = Phenol
MNOL = Methylated phenols
PCP = Pentachlorophenol
VOLA = Tetrachloroethene, ethylbenzene, total xylenes (analyzed for at 20
stations only)
BZAC = Benzoic acid (analyzed for at 126 stations only)
DBF = Dibenzofuran (analyzed for at 126 stations only)
BZOH = Benzyl alcohol (analyzed for at 126 stations only)
phth = Total phthalates
NPDA = n-Nitrosodiphenylamine
Tentatively Identified Compounds (analyzed for at 126 stations only)
APAH (alkyl PAH) = l,l'-biphenyl
2-methylphenanthrene
1-methylphenanthrene
1-methylpyrene
2-methylpyrene
DTP = Isopimaradiene (diterpene)
unidentified diterpene (possibly kaur-16-ene)
MEB = l-methyl-2-(l-methylethyl)benzene
RET = Retene
DIB = Dibenzothiophene
PCC = Pentachlorocyclopentane isomer
MOX = 2-methoxyphenol
COP = Coprostanol
b Stations with synoptic chemistry, sediment toxicity, and biological data.
c Station locations where chemical concentrations exceeded 90 percent of values
observed in Commencement Bay sediments are boxed.
3.77
-------
3.2 BENTHIC MACROINVERTEBRATES
3.2.1 Introduction
Benthic infauna are an integral part of the Puget Sound estuarine
ecosystem. They consume organic materials deposited on and in the sediments,
bioturbate the sediments, promote nutrient regeneration from the sediments,
and are prey of higher trophic level organisms. Benthic organisms are
relatively sedentary, and cannot avoid organic materials and chemical
contaminants that are deposited on the bottom. Because they are also sensitive
to organic enrichment and chemical contamination of the sediments, benthic
organisms are an excellent indicator group by which to assess the area!
extent and magnitude of environmental stresses (Pearson and Rosenberg 1978;
Wolfe et al. 1982).
The purpose of this section is to describe the general characteristics
of benthic communities in Commencement Bay waterways, along the Ruston-
Pt. Defiance Shoreline, and in the Carr Inlet reference area. An overall
characterization of benthic communities in Commencement Bay and Carr Inlet
is presented first, followed by qualitative comparisons of benthic communities
among and within these nine study areas. A numerical classification analysis
is then used to identify the major types of benthic communities and their
distributions among the study areas. Animal-sediment relationships are
explored with the aid of statistical analyses to identify sediment character-
istics that are important determinants of community structure within and
among the nine study areas. Statistical analyses are also used to develop
indices of benthic degradation that are later used as decision criteria
(Section 3.2.7). Finally, biological conditions observed during the present
study are compared with those observed in 1950, to determine whether benthic
biological conditions have changed since that time.
3.2.2 Characteristics of Benthic Communities in Commencement Bay and Carr
Inlet
During this study, 119,095 individuals belonging to 407 species were
collected from 56 sampling stations. The best represented major taxonomic
groups in the samples were the Polychaeta (marine worms), Bivalvia (clams),
Nematoda (round worms), Crustacea (e.g., amphipods and cumaceans), Echinodermata
(e.g., sea cucumbers and brittle stars), Oligochaeta (e.g., tubificid worms),
and Sipuncula (marine worms). Two species (i.e., the polychaete Tharyx
multifilis and the bivalve mollusc A x in o p s i da s er r i c a t a) accounted for
70,084 individuals or 59 percent of benthic organisms collected (Table 3.16).
Because of the preponderance of these two species, annelids and bivalve
molluscs were the two best represented major benthic groups. Nematodes
were the third most abundant major benthic because densities at a few stations
were extremely high. The fourth most abundant major group was the crustaceans,
represented primarily by the ostracods Euphilqmedes producta and E_. carcharo-
donta, and the tanaid Leptochelia dubia. Echinoderms and other major taxonomic
groups were present at low abundances in the samples. Ranked mean abundances
of benthic taxa at stations in Carr Inlet, and at stations in Commencement
Bay are given in Appendix XIII. Counts of infaunal species in each replicate
at each station are also listed.
3.78
-------
TABLE 3.16. ABUNDANCES AND RANKS OF THE 10 NUMERICALLY DOMINANT
BENTHIC TAXA COLLECTED IN COMMENCEMENT BAY
Taxona
Tharyx multifilis (Po)
Axinopsida serricata (Pe)
Nematoda
Macoma carlottensis (Pe)
Lumbrineris sp. gr. 1 (Po)
Capitella capitata (Po)
Euphilomedes producta (Os)
Euphilomedes carcharodonta (Os)
Leptochelia dubia (Ta)
Prionospio steenstrupi (Po)
Total
Abundance
42,106
27,978
9,784
4,351
4,018
2,771
2,289
1,836
1,242
1,148
Rank
1
2
3
4
5
6
7
8
9
10
Proportion
of Total
Individuals
0.354
0.235
0.082
0.037
0.034
0.023
0.019
0.015
0.010
0.010
Cumulative
Proportion
0.35
0.59
0.67
0.71
0.74
0.76
0.78
0.80
0.81
0.82
a Po = Polychaeta; Pe = Pelecypoda; Os = Ostracoda; Ta = Tanaidacea.
3.79
-------
3.2.3 Comparisons Among Study Areas
3.2.3.1 Numbers of Species--
Mean numbers of species (in some cases higher taxa) per grab sample
(i.e., per 0.06 m2) and mean numbers of individuals/m2 varied considerably
among the study areas (Figure 3.23). The highest mean numbers of species
were along the Ruston-Pt. Defiance Shoreline and in Carr Inlet, where they
averaged over 40 species per grab. Mean numbers of species in Hylebos,
Blair, Sitcum, Milwaukee, St. Paul, Middle, and City Waterways were about
35-50 percent lower, suggesting that some degree of stress was occurring
throughout the waterways, compared with adjacent habitats.
Tests for differences in numbers of taxa and numbers of individuals among
the nine study areas were conducted using the Kruskal-Wallis test [a nonpara-
metric analog of ANOVA (i.e., analysis of variance)]. This nonparametric
test was used in lieu of ANOVA because sample variances were highly hetero-
geneous (i.e., varied by a factor >10) in both data sets. Transformation
of the data using the relationship Y = logio(x+l) failed to reduce the
heterogeneity of the variances to an acceptable level. A posteriori multiple
range comparisons were conducted using the Mann-Whitney U-test, as recommended
by Winer (1971).
Results of the Kruskal-Wall is test and subsequent multiple range
comparisons indicated that numbers of taxa were generally depressed within
the waterways (Figure 3.23, Tables 3.17, 3.18). Numbers of taxa were
significantly higher (P<0.05) in Carr Inlet than in City, Hylebos, Milwaukee,
Sitcum, and St. Paul Waterways. The multiple range tests also indicated
that numbers of taxa at stations along the Ruston-Pt. Defiance Shoreline
were higher than at stations in Hylebos Waterway.
3.2.3.2 Total Abundances--
Total abundances (i.e., numbers of individuals/m2) also varied among
the nine Commencement Bay study areas (Figure 3.23). Abundances tended
to be higher in Blair, Sitcum, Milwaukee, and City Waterways than elsewhere.
A Kruskal-Wallis test detected statistically significant differences (P<0.05)
in abundances among the study areas. Subsequent a posteriori tests usinq
the Mann-Whitney U-test located statistically significant differences (P<0.05)
among 11 pairs of study areas. In general, abundances were higher (P<0.05)
in Middle and Sitcum Waterways, and lower (P<0.05) in St. Paul Waterway.
Extreme variations in abundances among the stations in City Waterway (discussed
below) may account for the absence of statistically significant differences
(P<0.05) in abundances between City Waterway and other study areas.
3.2.3.3 Numbers of Species and Abundances of Major Taxonomic Groups—
In general , trends in numbers of species and abundances for the major
taxonomic groups (i.e., Polychaeta, Mollusca, Crustacea, and Echinodermata)
were similar to those shown in Figure 3.23 for total numbers of species
and total abundances. High numbers of polychaete, mollusc, and crustacean
species (Figures 3.24, 3.25, 3.26) generally accounted for the high degree
of species richness found along the Ruston-Pt. Defiance Shoreline and in
Carr Inlet. Polychaetes were very abundant in the Hylebos, Blair, Sitcum,
3.80
-------
OJ
CO
Tl
c
-s
CJ
no
CJ
o» 3 3
-j ro n>
ft) QJ CD
O» 3 3
3 3
C C
3 3
CJ™ CT"
o> n>
-5 -S
0 O
-b -h
-J« (/)
^3 T3
Q- (D
-j. o
•~j« j*D
r> i/>
C
Cl) "O
— • (D
(/) -j
3 to
ro-s
O)
-'• cr
in
(T> CD
a> 3
0 XJ
(0
10
c
T
00
I—
CO
c
g co
-< T3
c? s
> o
o
33
CO
O
33
MEAN NO. SPECIES
MEAN NO. INDIVIDUALS/m2 PER GRAB SAMPLE (0.06 m2)
JO _O» jsj O N J^
i I i i I | f — *
I
03
CS
I
•^ "0
5 1
1 Q
33
CO
O
3)
1
1
1
-------
TABLE 3.17. RESULTS OF KRUSKAL-WALLIS TESTS COMPARING
NUMBERS OF TAXA PER GRAB SAMPLE AND NUMBERS OF INDIVIDUALS
PER GRAB SAMPLE AMONG THE STUDY AREAS3
Test
No. Cases
Chi-squareb
Significanceb
No. Taxa/Grab Sample
No. Individuals/Grab
Sample
192
192
44.00
38.48
0.0000
0.0000
a Each study area was characterized by the values of all replicates collected
therein.
b Probability that rank sums are approximately the same; corrected for ties.
3.82
-------
TABLE 3.18. RESULTS OF MANN-WHITNEY U-TEST MULTIPLE
COMPARISONS OF NUMBERS OF TAXA PER GRAB SAMPLE AND NUMBERS OF
INDIVIDUALS PER GRAB SAMPLE AMONG THE STUDY AREAS^
CI
BL nsb
CI
CR
HY
MD
MI
RS
SI
CI
BL ns
CI
CR
HY
MD
MI
RS
SI
No. Taxa/Grab
CR HY MD
ns ns ns
*c ns ns
* ns
ns
Sample
MI
ns
ns
*
ns
ns
No. Individuals/Grab Sample
CR HY MD MI
* ns ns
ns ns ns
ns ns
ns
ns
ns
*
*
ns
RS
ns
ns
ns
*
ns
ns
RS
ns
ns
ns
ns
ns
*
SI
ns
ns
*
ns
ns
ns
ns
SI
ns
ns
*
*
ns
ns
*
SP
ns
ns
*
ns
ns
ns
ns
ns
SP
*
ns
ns
*
ns
*
ns
*
a Each study area was characterized by the values of all replicates collected
therein.
D ns = not significant.
c Each test was considered significant (*) if P<0.00625. This significance level
is based on an experimentwise error rate of P<0.05 and eight pairwise comparisons
for each study area with all other study areas.
3.83
-------
CQ
40 T
20 •
HY BL SI Ml SP MD Cl RS
CR
STUDY AREA
y 55
I
12,000 -i
10,000 -
7,500 -
5,000 -
2,500 -
HY BL SI Ml SP MD Cl RS
CR
STUDY AREA
Figure 3.24.
Mean number of polychaete species per grab
sample and mean number of polychaete indi-
viduals^ in each survey area.
3.84
-------
OJ
00
en
-n
c
-i
co
ro
en
fl> ai 3:
O) 3 fD
C/> fD 3
c o c
fD 3 fD
<< c -s
-S ffc -h
fD T
O) 3
• O O
O (/>
—> O
C I/)
o o>
n
3 fD
OL V
< T3
cx -s
CU IT)
(/> OJ
row
3 "O
n>
I
CO
CO
C/5 ~
H
TI
m 2
> 0
0
33
O
33
MEAN NO. MOLLUSC
INDIVIDUALS/m2
-* M g A pi p>
X
CD
CO
I
-H
§ 3
>
5 §
O
33
CO
O
33
MEAN NO. MOLLUSC
SPECIES PER GRAB
SAMPLE (0.06 m2)
i i
-------
S< sr
3CC P
oc ai 2,
oo- m
*u
Z LU <
20 -i
10-
I
in
r-i
HY BL SI Ml SP MD Cl RS
CR
STUDY AREA
2,000 -t
O ^
ll
03
iSi
n
i — i
1 U
HY BL SI Ml SP MD Cl RS
CR
STUDY AREA
Figure 3.26.
Mean number of crustacean species per grab
sample and mean number of crustacean indi-
viduals^ in each survey area.
3.86
-------
Milwaukee, Middle, and City Waterways, while molluscs were very abundant
in the Blair, Sitcum, and Milwaukee Waterways. Polychaetesand molluscs
accounted for generally enhanced total numerical abundances in the waterways.
Echinoderms exhibited low numbers of species and low abundances in all
study areas (Figure 3.27).
3.2.3.4 Numerically Abundant Taxa--
Abundances of the five most abundant taxa (i.e., the numerically dominant
taxa) in each study area are summarized in Figure 3.28 and Table 3.19.
(The data in Figure 3.28 and Table 3.19 are combined for all stations within
a study area and are intended to give an overview of conditions within
each study area. Taxonomic composition and abundances differed among the
stations within many of the study areas, and will be discussed below.)
Very high dominance (i.e., 63-95 percent) was exhibited by benthic communities
in all study areas except the Ruston-Pt. Defiance Shoreline (i.e., 36 percent)
and Carr Inlet (i.e., 44 percent). High dominance values may indicate
stressed conditions, since less tolerant species are eliminated and opportun-
istic species tend to achieve high abundances (Pearson and Rosenberg 1978;
Gray 1982).
Taxonomic composition and, hence, the feeding modes of the dominant
species differed considerably among the study areas (Figure 3.28, Table 3.19).
For all stations combined, the Hylebos, Blair, Sitcum, Milwaukee, and,
to a lesser degree, Middle Waterways were dominated by the surface deposit-
feeding polychaete Tharyx multifilis and the surface detritus-feeding bivalve
mollusc Axi'nopsida serricata (see Fauchald and Jumars 1979; Word 1980).
These two species have not been identified in the scientific literature
as being opportunistic. The St. Paul and City Waterways (for all stations
combined) were dominated primarily by subsurface deposit-feed ing nematodes.
The subsurface deposit-feeding polychaete Capitella c_a_p_Tt_ata_ was the second
most abundant taxon in the St. Paul Waterway and the fourth most abundant
taxon in Middle Waterway (after nematodes, J_. multifili^s, and A_. serricata).
(Note that nematodes and Capitella capitata are not the most abundant taxa
throughout either the St. Paul or City Waterways, but are extremely abundant
only at certain stations. This will be discussed below.) Both nematodes
and the polychaete C. capitata^ are known to reach very high abundances
in organically enrTched sedTments, often to the near exclusion of other
taxa (Nichols 1972; Pearson and Rosenberg 1978; Van Es et al. 1980). The
dominance of these two taxa suggests that some sediments in St. Paul and
City Waterways are organically enriched.
3.2.3.5 Contaminant-Sensitive Taxa--
Many echinoderm and crustacean species are sensitive to contaminants
and environmental disturbance (Reish and Barnard 1979; Word 1978, 1980).
Although numbers of echinoderm species and abundances of echinoderms were
too low in all of the study areas for useful inter-area comparisons (Figure
3.27), abundances of amphipods (i.e., sensitive crustaceans) may be compared
among study areas. Data in Table 3.20 indicate that amphipods were abundant
only in Carr Inlet and along the Ruston-Pt, Defiance Shoreline, excluding
Station RS-18. A one-way ANOVA was conducted to test for differences in
mean amphipod abundances among all Commencement Bay study areas and Carr Inlet
using the data in Table 3.20. Middle Waterway was deleted from the analysis
3.87
-------
00
-n
— j*
IQ
C
-5
0>
U)
ro
-vl
C -0 3
OJ — "
, fr* «•
— • ID 3
«/l C
^. O> 3
33CT
roo. co
-j
3 fB O
O) -h
fD 3
CD fy
n 3 o
3" C 3"
t/^ C^ 3
c* fD O
c ~i o.
«< o 3
-h 3
cu
•j n> f
fD O T3
CU 3- fD
. _i. o
3 -*•
o n>
CX to
o>
-s
Z3 ^Q
f^_. ~^j
i cr
MEAN NO. ECHINODERM
MEAN NO. ECHINODERM SPECIES PER GRAB
INDIVIDUALS/m2 SAMPLE (0.06 m2)
•^ W
8O k%
O O -* W
II 1 *
I
CO
CO
^
—
CO
C CO
.^
1 1
o
3J
CO
o
JJ
: 5
J "
CO
"~j s
CO
C CO
Q "0
"V
^^
51 D
•M
~
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1 33
J W
1 o
1 3D
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D
— — 1
_MW— J
-------
14,000 -
12,000 -
c
E
M 1°'°00'
3
>
Q
u.
O
CC
111
00
;g
2 6,000 -
4,000-
2,000 -
n
5
4
3
1
84%
3
5
6
1
83%
3
7
6
2
1
95%
7
2
1
84%
1
10
y
s
63%
?
B
11
1
78%
11
2
1
8
79%
ODTO
16 44%
15 17 | 1
15
1 2
13 10
HY BL SI Ml SP MD Cl RS
STUDY AREA
CR
NUMBERS BESIDE THE BARS REFER TO SPECIES LISTED IN TABLE 3.19.
Figure 3.28.
Mean abundances per station of the five nu-
merically dominant species per study area and
the proportions of total infaunal abundances
for which they account.
3.89
-------
TABLE 3.19. KEY FOR FIGURE 3.28
1 = Tharyx multifills (Polychaeta)
2 = Axinopsida serricata (Pelecypoda)
3 = Lumbrineris sp. gr. 1 (Polychaeta}
4 = Cirratulus cirratus (Polychaeta)
5 = Euphilomedes producta (Ostracoda)
6 = Macoma carlottensis (Pelecypoda)
7 = Lumbrineris luti (Polychaeta)
8 = Nematoda
9 = Capitella capitata (Polychaeta)
10 = Leptochelia dubia (Isopoda)
11 = Cossura soyeri (Polychaeta)
12 = Nephtys cornuta franciscana (Polychaeta)
13 = Mediomastus spp. (Polychaeta)
14 = Euphilomedes carcharodonta (Ostracoda)
15 = Prionospio steenstrupi (Polychaeta)
16 = Phyllochaetopterus prolifica (Polychaeta)
17 = Scalibregma inflatum (Polychaeta)
3.90
-------
TABLE 3.20. NUMBERS OF AMPHIPODS COLLECTED AT EACH OF THE
COMMENCEMENT BAY STATIONS (0.24-m2) SAMPLED IN MARCH, 1984
Station
HY-12
HY-14
HY-17
HY-22
HY-23
HY-24
HY-28
HY-32
HY-37
HY-42
HY-43
HY-44
HY-47
HY-50
BL-11
BL-13
BL-21
BL-25
BL-28
BL-31
SI-11
SI-12
SI-15
MI-11
MI-13
MI-15
Abundance
0
0
1
6
0
3
10
2
2
1
5
6
1
6
1
3
0
1
8
1
1
2
4
2
1
3
Station
SP-11
SP-12
SP-14
SP-15
SP-16
MD-12
CI-11
CI-13
CI-16
CI-17
CI-20
CI-22
RS-12
RS-13
RS-14
RS-18
RS-19
RS-20
CR-11
CR-12
CR-13
CR-14
Abundance
25
17
1
1
4
0
2
1
0
1
0
0
16
200
72
0
29
45
65
14
39
167
3.91
-------
because there was only one data point for number of amphipods; a minimum
of two points is necessary to estimate the mean and standard deviation.
The test found mean abundances to be significantly different (P<0.05) among
the study areas. A subsequent Student-Newman-Keuls multiple comparison
test yielded two nonsignificant subsets of stations, based on a statistical
significance level of P<0.05. Subset one consisted of the Hylebos, Blair,
Site urn, Milwaukee, St. Paul, and City Waterways, while subset two consisted
of the Ruston-Pt. Defiance Shoreline and Carr Inlet. These results further
substantiate the hypothesis that amphipod abundances are depressed in the
waterways relative to the Ruston-Pt. Defiance Shoreline and Carr Inlet.
Because many amphipod species are sensitive to contaminants, organic
enrichment, and environmental disturbance (Bellan-Santini 1980; Swartz
et al. 1982b; Oakden et al. 1984), it is probable that one or more of these
factors contributed to the depressed amphipod abundances observed in the
waterways. Alternatively, the naturally occurring sandy sediments found
along the Ruston-Pt. Defiance Shoreline and in Carr Inlet might be expected
to support larger amphipod populations than the muddy sediments found in
the Comnencement Bay waterways. A correlation analysis of amphipod abundances
at stations within the waterways (Ruston-Pt. Defiance Shoreline and Carr Inlet
excluded) with percent sand in the sediments was conducted during this
review. Results were highly significant (P<0.0001). Thus, the lower amphipod
abundance observed in the Commencement Bay waterways may be due to one
or more of types of environmental stress, or to differences in sediment
characteristics.
3.2.4 Comparisons Within Study Areas
Considerable variation in numerical abundances and species composition
occurred within each study area (Figures 3.29-3.32, Table 3.21). For example,
benthic communities along the Hylebos Waterway were dominated by Tharyx
multifilis and Axinopsidaserricata, but abundances of those two species
combined varied from 137 to 14,546/m2 among the stations (Figure 3.29).
Abundances of the five numerically dominant species exceeded 4,0007m2 at
most stations, but were depressed below this value in the vicinity of Stations
HY-22, HY-23, HY-32, HY-37, and HY-44. Greatly depressed abundances often
indicate excessively enriched sediments or the presence of contaminants
(Pearson and Rosenberg 1978; Carriker et al. 1982; Wolfe et al. 1982; Dillon
1984). The Tharyx-Axinopsida community also occurred throughout Blair,
Sitcum, and Milwaukee Waterways. Abundances of the five numerically dominant
taxa were less variable within each of these waterways than were those
observed in Hylebos Waterway (Figure 3.30), and all but Station BL-28 (near
the East llth Street Bridge) exhibited abundances of 8,000/m2 Or greater.
The benthic community at the single station in Middle Waterway also
was dominated by Tharyx multifil is, with Axinopsida serricata present as
the fifth most abundant taxon (Figure 3.31). Total abundance of the five
most abundant taxa was somewhat lower at the station in Middle Waterway
than was typical of those in Blair, Sitcum, and Milwaukee Waterways (5,588/m2).
Stations in St. Paul Waterway supported very different benthic communities
than those observed in the waterways north of the Puyallup River (Figure 3.31).
At none of the St. Paul Waterway stations was a Tharyx-Axinppsida community
found. Nematodes and the polychaete Capitella capvEata were the most abundant
3.92
-------
10
u>
20,000 -
CM
ci icnnn -
O
i_
1
CC 12,000 -
UU
Q_
(/)
^
-J
QJ
Q
Z
LL
0
£ 4,000-
CQ
r>
0
5
3
1
92%
fi
s
1
92%
2
e
7
1
94
-------
20,000 -
Cj 16,000 -
E
CO
Q 12,000 -
Q
2
LL
O 8000 -
OC
UJ
5
ID
4,000 -
0
17
3
5
2
1
92%
I— —I
5
1
^
80%
4
5
3
91%
5
4
a
2
88%
18
3
5
1
2
90%
3
5
1
2
87%
-
-
.
4
3
5
2
83%
3
5
2
1
96%
1°
3
2
1
97%
4
5
3
2
92%
s
2
91%
3
12
2
1
8/%
BL-31 BL-28 BL-25 BL-21 BL-13 BL-11
SI-15 SI-12 SI-11
MI-15 MI-13 MI-11
STUDY AREA
NUMBERS BESIDE THE BARS REFER TO SPECIES LISTED IN TABLE 3.21.
Figure 3.30. Total abundances of numerically dominant species at stations in Blair,
Sitcum, and Milwaukee Waterways, and the proportions of total infaunal
abundances for which they account.
-------
CO
vO
tn
20,000 -
16,000 -
CM
CO
Q 12,000 -
Q
Li.
° 8,000 -
cc
LJ
m
— \
4,000 -
0
1
8
21
20
3
60%
24
1
*
QPOA
8 9
25 21
11^^^^ 26
42%
21
1
30
29
28
63%
_
-
-
"
2
3
1
7fl%
P^H^W^
_
-
-
12
8
3
2
82%
1?
R
3
1
83%
____
2
12
31
1
81%
*
27
32
22
20
81%
33
1
29
20
22
;
3
30
32 72%
99%
Y\
- 44,000
- 40,000
ico
i Q
m >
m i—
- 36,000 ^ m
o 3
DO
Z CO
5 £j
- 32,000 o O
^ ^
r~ ^}
•2 :i
1 -
SP-16 SP-15 SP-14 SP-12 SP-11
MD-12
CI-22 CI-20 CI-17 CI-16 CI-13 CI-11
STUDY AREA
# CROSS WATERWAY TRANSECT
NUMBERS BESIDE THE BARS REFER TO SPECIES LISTED IN TABLE 3.21.
Figure 3.31. Total abundances of numerically dominant species at stations in
St. Paul, Middle, and City Waterways, and the proportions of total
infaunal abundances for which they account.
-------
O>
20,000 -
16,000 -
CO
12,000 -
O 8,000
oc
LU
CD
4,000 -
700/0
43%
35, .17
29
28
440A
% «g*,8<
41
6
40
17 35%
"H
43
66%
46 56%
48 59% 50
RS-12 RS-13 RS-14 RS-18 RS-19 RS-20
CR-11 CR-12 CR-13 CR-14
CROSS WATERWAY TRANSECT
NUMBERS BESIDE THE BARS REFER TO SPECIES LISTED IN TABLE 3.21.
Figure 3.32. Total abundances of the numerically dominant species at stations along
the Ruston-Pt. Defiance shoreline and in Carr Inlet and the proportions
of total infaunal abundances for which they account.
-------
TABLE 3.21. KEY FOR FIGURES 3.29 THROUGH 3.32
1 = Tharyx multifilis (Polychaeta)
2 = Axlnopslda serrlc'ata (Polychaeta)
3 = Macpma carlottensis (Pelecypoda)
4 = Euphilomedes producta (Ostracoda)
5 = Lumbrineris sp. gr. 1 (Polychaeta)
6 = Cirratulus cirratus (Polychaeta)
7 = Psephidia lordj (Pelecypoda)
8 = Euphilomedes carcharodonta (Ostracoda)
9 = Macoma obliqua (Pelecypoda)
10 = Lumbrineris sp. gr. 3 (Polychaeta)
11 = Prionospio steenstrupi (Polychaeta)
12 = Chaetozone spp. (Polychaeta)
13 = Odostomia spp. (Gastropoda)
14 = Cos sura s~pp. (Polychaeta)
15 = Euchone sp. A (Polychaeta)
16 = Plsta cristata (Polychaeta)
17 = Notomastus tenuis (Polychaeta)
18 = Prax ill el la gracilis (Polychaeta)
19 = Glycera capitata (Polychaeta)
20 = Capitella capitata (Polychaeta)
21 = Nephtys cornuta^ franciscana (Polychaeta)
22 = Nematoda
23 = Schistomeringos rudolphi (Polychaeta)
24 = Gyptis brevipalpa (Polychaeta)
25 = Cancer sp. (Decapoda)
26 = Nephtys^ cornuta (Polychaeta)
27 = Macoma nasuta (Pelecypoda)
28 = Leptochelia dubia (Tanaidacea)
29 = Platynereis ^icaniculata (Polychaeta)
30 = Macoma nasutli (Pelecypoda)
31 = Prionospio cirrifera (Polychaeta)
32 = Armandia breyis (Polychaeta)
33 = Tubificidae (01igochaeta)
34 = Mediomastus^ spp. (Polychaeta)
35 = Phot is breVipes (Amphipoda)
36 = Prionospio multibranchiata (Polychaeta)
37 = Leptostylis villosa (Cumac'ea)
38 = Limnoria lignorum (Isopoda)
39 = Amphipholis squamata (Ophiuroidea)
40 = Balanuj crenatus (Cirripedia)
41 = Pajeonotus bell is (Polychaeta)
42 = Pseudochftinopoma occidental 1_s_ (Polychaeta)
43 = PhyllochaetopterlTs prolifica
44 = Pplydora spp. (Polychaeta)
45 = PhoTolde's aspera (Polychaeta)
46 = Amphiodi'a urtica (Ophiuroidea)
47 = Scalibregma inflatum (Polychaeta)
48 = Mitrella gouTdi (Pelecypoda)
49 = CapreVlidae (Amphipoda)
50 = Caprella mendax (Amphipoda)
3.97
-------
taxa at Station SP-15 in the outer portion of the waterway. These two
taxa contributed most of the organisms collected at that station and were
present at a combined abundance of more than 8,000/m2. AS discussed above,
the numerical dominance of nematodes and C_. capitata may indicate highly
enriched sediments. The remaining four stations were dominated by an assortment
of polychaete, mollusc, and crustacean species, all of which occurred at
low combined abundances (<4,000/nr). Abundances of the five numerically
dominant species at Station SP-14, inshore of Station SP-15, were especially
depressed (92/m2), suggesting that a high level of stress was occurring
at that station. The very different suites of species among the St. Paul
Waterway stations suggest that sediment conditions were highly localized
and varied over short distances.
Benthic communities along the length of City Waterway changed markedly
in species composition and abundances. Station CI-11, at the head of the
waterway, was a nematode-Capitella capitata community in which the abundances
of nematodes alone exceeded 32,000/m?tAt Stations CI-13 and CI-16, towards
the mouth of the waterway, abundances of the numerically dominant taxa
become very reduced (<4,000/m2). Tharyx multifJHs was the most abundant
taxon at Station C-13, while C. c a pi t at a a rid n ema t od e s were the two most
abundant taxa at Station C^BT Stations CI-17, CI-20, and CI-22 in the
outer half of the City Waterway were dominated by T. multifilis and Axinopsida
serricata. Combined numerical abundances of The dominant taxa were about
8,OoO/m2 or greater, as was typical of Tharyx-Axinopsida communities in
Blair, Sitcum, and Milwaukee Waterways. Changes in species compositions
and abundances within City Waterway suggest that the greatest environmental
stresses occurred near the head of the waterway, and that conditions improved
toward the mouth of the waterway.
Along the Ruston-Pt. Defiance Shoreline, the Tharyx-Axinopsida corrounity
typical of the waterways was found only at Station RS-12, located near
City Waterway. Species composition varied at the remaining stations along
the shoreline. The most striking aspect of the data in Figure 3.32 is
the reduced abundances of benthic organisms at Stations RS-19 and RS-20,
and the nearly abiotic sediments collected at Station RS-18. Of the four
replicate benthic grab samples collected at Station RS-18, only two contained
any macroinvertebrates (i.e., a total of seven organisms). The virtual
absence of benthic biota in the vicinity of Station RS-18 is indicative
of severe stress.
3.2.5 Classification Analyses
3.2.5.1 Introduction--
Numerical classification analyses group entities (in this case stations)
based on their attributes (in this case abundances of the 64 most abundant
taxa collected in the study). They are effective because they reduce complex
data sets to groups of entities with similar, and therefore interpretable,
characteristics.
The classification analysis conducted during this study involved two
steps. The first was to generate similarity values for all possible pairs
of stations included in the analysis. The Bray-Curtis Similarity Index
(see Boesch 1977) was employed for this purpose. It uses both species
3.98
-------
composition and abundances of the individual species to estimate between-
site similarity. The group average clustering strategy was then applied
to the matrix of similarity values to generate a dendrogram of stations
(Figure 3.33). Groups of stations (i.e., stations that are most similar
in species composition and abundance) may then be determined based on selected
similarity levels.
Ideally, a single similarity value should be selected (albeit somewhat
subjectively) and all station groups should be determined relative to that
value. However, a single similarity level does not yield interpretable
station groups when the dendogram exhibits excessive "chaining", or sequential
additions of stations or station pairs to the most similar group of stations,
as in Figure 3.33. Therefore, several similarity levels have been selected
in the following interpretation of the data in Figure 3.33.
Although 56 stations were sampled during this survey, only data from
54 stations were used in the classification analysis and statistical analyses
conducted during this study. Steep bottom topography and very sandy sediments
were encountered at the remaining two stations off Pt. Defiance, so that
it was impossible to collect representative 0.06-m2 (0.6-ft^) grab samples.
Therefore, those two stations were deleted from further consideration.
3.2.5.2 Results--
Results of a normal (Q-mode) classification analysis using abundances
of the 64 numerically dominant species in the Commencement Bay study areas
are shown in Figures 3.33 and 3.34. The dominant species within these
station groups, their mean abundances, and mean total volatile solids (TVS)
and total organic carbon (TOC) concentrations for the stations in each
station group are given in Table 3.22. Sediment grain size characteristics
of the major station groups are summarized in Figure 3.35.
3.2.5.3 Interpretation--
Included in Group 1 were the Blair Waterway stations (except BL-28
near the outer bridge and BL-31 near the mouth of the waterway), the Milwaukee
Waterway stations, the two inner stations in the Sitcum Waterway, and Station
HY-50 off the mouth of the Hylebos Waterway. The two co-dominant species,
Axinopsida serricata and Tharyx multifi1 is, accounted for most of the
individuals collected. Sediments within Group 1 were primarily sandy silts,
with moderate organic levels (x=5.0 percent TVS, x=1.8 percent TOC).
Group 2 was also dominated by Tharyx mult if i 1 is and Axinopsida serricata,
but abundances of A. serricata were about five times lower than those of
J_. multifilis. Group 2 included four stations in the outer third of the
Hylebos Waterway, Station BL-31 near the mouth of Blair Waterway, and Station
HY-24 in upper Hylebos Waterway. The stations in Group 2 had slightly
greater quantities of clay than the stations in Group 1, but the major
difference was the increased quantities of organic materials (x=6.3 percent TVS,
x=2.6 percent TOC) compared with Group 1 (x=5.0 percent TVS, x=1.8 percent TOC).
Station BL-28 near the llth Street Bridge was an outlier to Groups
1 and 2. It was also co-dominated by Axinopsida serricata and Tharyx
multifilis, but at relatively low abundances"!the proximity of Station BL-28
3.99
-------
% DISSIMILARITY STATION
100. 90.0 80.0 70.0 60.0 50.0 40.0 30.0 20.0 10.0 .00
II I I i i i I
J
rf
— c
rl
1 — L
. 1
| 1
H
i — i
1
L| 1=
L| L
I i , n, .-,
n i — ' B ?
1 ,_ R q
HI — l = . « 1
I . i al 11
J SI - IS
i HY - 12
1 — HY - 14
„„--, HY - 22
, SP 11 £-
1 SP 12 U
. .- - CR 11 Q
.: - .. CR 11
RS 13 -.
RS 14 '
D 11— T-
SP 15 °
1 1 | i l i l 1 i i 1
100. 90.0 80.0 70.0 60.0 50.0 40.0 30.0 20.0 10.0 .00
% DISSIMILARITY STATION
DOMINANT SPECIES ARE LISTED IN TABLE 3.22
COPHENIC CORRELATION COEFFICIENT: .9454
Figure 3.33. Results of a Q-mode classification analysis (Bray-Curtis
similarity index, group average clustering strategy) using
square-root transformed abundances of the 64 numerically
dominant infaunal species.
3.100
-------
COMMENCEMENT
BAY
PERCENT TOTAL
VOLATILE SOLIDS
LESS THAN 2
2-4
4-6
6-8
8-10
10-12
12-14
OVER 14
0 4000
I I I I I FEET
T
1 METERS
.^. o 1000
Qf«m DOMINANT TAXA FOR EACH GROUP ARE LISTED IN TABLE 3.22.
Figure 3.34.
CITY
WATERWAY
Geographic distribution of station groups 1-9,
plus outliers (o), in Commencement Bay water-
ways (from Figure 3.33). (Note: group boun-
daries are uncertain.)
-------
TABLE 3.22. MEAN ABUNDANCES (No./m2) OF NUMERICALLY DOMINANT TAXA
AND MEAN VALUES OF SEDIMENT CHARACTERISTICS FOR THE MAJOR STATION GROUPS
DEFINED BY NORMAL CLASSIFICATION ANALYSES (SEE FIGURE 3.33)
Station
Group
1
2
3
4
5
6
7
8
Out! iers
BL-28
CR-12
HY-23
RS-20
RS-18
SP-14
RS-19
Taxon
Axinopsida serricata
Tharyx multifilis
Macoma carlottensis
Lumbrineris sp. gr. 1
Euphilomedes producta
Tharyx multifilis
Axinopsida serricata
Lumbrineris sp. gr. 1
Euphilomedes producta
Macoma carlottensis
Tharyx multifilis
Axinopsida serricata
Macoma carlottensis
Nephtys cornuta franciscana
Tharyx multifil is
Lumbrineris sp. gr. 1
Tharyx multifil is
Macoma carlottensis
Nephtys cornuta franciscana
Leptochelia dubia
Prionospio steenstrupi
Axinopsida serricata
Mediomastus spp.
Platynereis bicaniculata
Prionospio steenstrupi
Leptochel ia dubia
Odostomia spp.
Tubificidae
Nematoda
Capitella capitata
Axinopsida serricata
Tharyx multifilis
Macoma carlottensis
Lumbrineris sp. gr. 1
Axinopsida serricata
Euphilomedes carcharodonta
Prionospio steenstrupi
Axinopsida serricata
Tharyx multifil is
Phyllochaetopterus pro! ifica
Polydora spp.
Leptostylis villosa
Limnoria lignorum
Amphipholis squamata
Nematoda
Tharyx multifilis
Balanus crenatus
Cirratulus cirratus
Paleonotus bellis
Total Volatile
Abundance/m2 Solids (%)
7 c.v.a 7 c.v.
5,357
4,837
745
612
348
6,453
1,362
438
242
135
5,833
603
378
220
3,152
252
397
192
148
660
315
288
1,273
808
707
453
270
210
19,823
4,548
1,258
495
412
308
792
420
325
217
75
337
200
4
4
4
45
20
775
470
217
55.5 5.0 45.5
64.3
75.3
67.4
86.7
47.0 6.3 41.8
63.9
40.8
47.4
45.0
62.1 9.0 47.3
79.4
18.9
52.8
37.6 10.3 18.8
29.3
73.4 8.3 60.1
81.0
87.6
151.4 1.1 0.3
72.4
94.8
2.0 15.6 59.2
56.0
86.0
53.0
30.0
1.0
101.5 8.9 73.1
37.8
1.9
0.3
10.5
1.5
19.6
44.3
1.0
Total Organic
Carbon (%)
"x c.v.
1.8 46.1
2.6 47.5
3.8 35.2
4.7 15.6
4.5 84.0
0.3 32.3
7.9 129.0
5.5 88.1
0.7
0.03
3.8
0.3
8.8
1.6
0.6
a c.v. = coefficient of variation. 7 in?
-------
SAND AND GRAVEL
SILT
CLAY
DOMINANT SPECIES FOR STATION GROUPS ARE LISTED IN TABLE 3.22.
Figure 3.35.
Sediment grain size characteristics of the
major station groups defined by normal classi-
fication analysis of the benthic infaunal data
in Commencement Bay study areas.
3.10;
-------
to bridge supports, the silty sand substrate found at that station, and
the lower levels of organic materials (x=1.9 percent TVS, x=0.7 percent
TOC) suggest that sediment scouring occurs there. Field observations of
scoured sediments near these bridges indicate that passing barges have
scraped bottom. Such physical disturbance may account for the differences
observed between Station BL-28 and Station Groups 1 and 2.
Sediments near the terminus of Hylebos Waterway (Station Group 4)
contained much greater quantities of organic materials (x=10.3 percent TVS,
x=4.7 percent TOC) than did stations near the mouth (Station Groups 1 and 2).
Faunal composition also changed. With the exception of Station HY-12 near
the terminus of the Hylebos Waterway, Tharyx mulifilis dominated benthic
communities in the upper third of the waterway, in the absence of high
abundances of Axinopsida serricata.
Groups 3 and 5 and outlier Station HY-23 occur in the middle reaches
of the Hylebos Waterway. Silty clay sediments were found at Station HY-23
and silty sand sediments were found at stations in Groups 3 and 5. The
sediments of Groups 3 and 5 and Station HY-23 were characterized by relatively
high levels of organic materials (x TVS=8.3-10.5 percent, x TOC=3.8-4.5
percent), as were the sediments of the upper waterway (Station Group 4).
Station HY-23 and the stations in Group 5 were all characterized by low
abundances of the dominant taxa. Abundances of Axinopsida serricata and
Inaryx mult if 111s were particularly low at Station HY-23, averaging 13/m2
and 75/m-i, respectively. Generally, abundances of A. serricata decreased
and abundances of J_. multifilis increased from the mouth of the waterway
to the upper turning basin. Relative changes in the abundances of these
two species along the waterway appear to have provided the discrimination
between Groups 3, 4, and 5, and Station HY-23. Major changes in species
composition were not apparent.
Group 6 included all Carr Inlet stations except CR-12, which was an
outlier. Group 6 stations were characterized by sandy sediments with low
organic levels (x=l.l percent TVS, x=0.3 percent TOC). The tanaid Leptochelia
dubia, the polychaete Prionpspio steenstrupi, and the bivalve mollusc Axinopsi^a"
serricata were the numerical dominants in station Group 6. While /\. serricata
was abundant at many of the Commencement Bay waterway stations, L. dubia
and £. steenstrupi were not. The abundance of these two latter species
distinguishes Stations CR-11, CR-13, and CR-14 (Group 6).
Group 7 consisted of Stations RS-13 and RS-14 along the Ruston-Pt. Defiance
Shoreline. Sediments at these two stations were highly enriched sands
(x=15.6 percent TVS, x=7.9 percent TOC), and the benthic communities were
dominated by the polychaetes Mediomastus spp. and Platynereis bicaniculata.
These two species were not co-dominants at any other station sampled during
the present study.
Group 8 consisted of only Station CI-11 at the head of City Waterway
and Station SP-15 in the outer reaches of St. Paul Waterway. Both stations
were dominated by nematodes and the polychaete Capitella capitata. which
occured at very high abundances (combined abundances >B,WQ/HP). Sediments
at these two stations were silty sands with relatively high proportions
of TVS (x=8.9 percent) and TOC (x=5.5 percent).
3.104
-------
Faunal and sedimentary characteristics documented at Station SP-15
and CI-11 are better understood by comparisons with adjacent stations.
In outer St. Paul Waterway, nearshore Station SP-14 (an outlier) exhibited
very low abundances. Sediments at Station SP-14 were principally wood
chips with silt, characterized by very high levels of organic materials
(44.7 percent TVS, 16.0 percent TOC). Farther offshore at Station SP-15,
sediments were primarily wood chips with sand, and organic materials were
present at lower concentrations (8.9 percent TVS, 5.5 percent TOC). Sediments
at Station SP-16 were sandy silt with yet lower concentrations of organic
materials (3.6 percent TVS, 1.5 percent TOC). Coincident with the reductions
in wood chips and quantities of organic materials from Station SP-14 to
Station SP-16, abundances of infaunal organisms increased. Almost no organisms
occurred at Station SP-14. Nematodes and the polychaete Capitella capitata
were abundant and numerically dominant at Station SP-15, while farther
offshore at Station SP-16, the bivalve mollusc Macoma carlottensis and
the polychaete C_. capitata were numerically dominant. Thus, there appears
to have been a severe negative impact in the vicinity of Station SP-14,
with conditions improving offshore. This impact also appears to have extended
into the St. Paul Waterway as evidenced by the low abundances recorded
at Stations SP-11 and SP-12. Sediments at Stations SP-11 and SP-12 were
partially composed of wood chips and exhibited high concentrations of TVS
(7.9-8.6 percent) and TOC (3.5-4.7 percent). As in most of the waterways,
the polychaete Tharyx multifilis was numerically dominant. However, in
contrast to the other waterways, it occurred only in low abundances, a
possible indication of stress.
A similar gradation of sediment characteristics and species composition
occurred along the length of City Waterway. Highest sediment organic levels
occurred at Stations C-ll, C-13, and C-16 (x=11.4-17.3 percent TVS, x=6.5-10.9
percent TOC). Nematodes and Capitella capitata dominated the communities
at Stations C-ll and C-16, and were extremely abundant at Station C-ll.
As noted earlier, these taxa may reach high densities in areas of high
organic enrichment. Tharyx multifilis occurred in place of nematodes and
C_. capitata at Stations C-13 and C-17. It occurred in much higher densities
at Station C-17 (25,150/m2) than at Station C-13 (l,433/m2). Communities
at these stations appeared to be transitional between those of Station
CI-11 in the upper waterway and Stations CI-20 and CI-22 in the lower waterway.
Lower waterway Stations CI-20 and CI-22 contained less organic material
(x=3.2-8.5 percent TVS, x=1.2-4.6 percent TOC) in the sediments than did
upper waterway Station CI-11 (13.5 percent TVS, 8.9 percent TOC) and were
dominated by Axinopsida serricata and T. multifilis. Stations CI-20 and
CI-22 were included in Group 1, which inHTcates that the communities in
lower City Waterway were similar to those elsewhere in the waterways where
organic enrichment was moderate and other possible sources of stress (e.g.,
toxic substances) apparently were not severe.
The four most unique stations sampled during the present survey were
the outlier Stations HY-23, SP-14 (nearshore in the outer reaches of St. Paul
Waterway), RS-18, and RS-19. All but Station RS-19 exhibited very low
numerical abundances (<2,100/m2). Tharyx multifilis and Axinopsida serricata
were the two most abundant taxa at Station HY-23, but the remaining thf'ee
stations were dominated by an assortment of polychaete, mollusc, and crustacean
species that were absent, or occurred at very low abundances, at other
stations in Commencement Bay and Carr Inlet (Figures 3.29-3.32). Very
3.105
-------
low numerical abundances, unique combinations of numerically dominant taxa,
or both accounted for the uniqueness of these stations in the results of
the classification analysis.
Sediment grain size characteristics at the low-abundance stations
(i.e., Stations HY-23, SP-14, and RS-18) ranged from clayey silt to silty
sand. TVS and TOC content of the sediments also varied considerably (3.7-19.6
percent and 1.6-8.8 percent, respectively). The only major common character-
istic which these stations shared was greatly depressed abundances of benthic
organisms compared with the other stations sampled during the study. As
noted earlier, very reduced abundances indicate stressed conditions.
3.2.6 An imal-Sed iment Relationshi ps
As noted earlier, sediments were sandy along the Ruston-Pt. Defiance
Shoreline and in Carr Inlet, whereas silty sands and sandy silts predominated
in the waterways (Figure 3.35). Changes in water depth, volatile solids
content (Figure 3.36), total organic carbon content (Figures 3.37, 3.38,
3.39), and the proportion of fine-grained materials (silt plus clay) in
sediments (Figures 3.40, 3.41, and 3.42) were also evident within and among
the study areas. While excess organic materials and other pollutants (e.g.,
toxic substances) affected species composition and abundance of benthic
infauna within each study area, the affinities of benthic species for particular
water depths and sediment habitats cannot be ignored.
The affinities of major taxonomic groups for particular sediment charac-
teristics are clearly illustrated by the data in Figure 3.43. Total numerical
abundances of all benthic species, polychaetous annelids, and molluscs
are all significantly (P<0.01) correlated with the proportion of fine materials
in the sediments.
Percent volatile solids, percent total organic carbon, percent sand,
percent silt, and percent clay were all tested against abundances of the
major taxonomic groups and selected dominant taxa. The grain size variables
appeared to explain a substantial proportion of the variations in numerical
abundances of benthic organisms (Table 3.23). Abundances of oligochaetes,
amphipods, and Prionospio spp. were all positively correlated with percent
sand and negatively correlated with percent silt or clay. Conversely,
abundances of polychaetes, molluscs, Lumbrineris spp., Axinopsida serricata,
and Macoma _ca_r1ottensi_s_ were positively correlated with percent silt or
silt plus clay, and negatively correlated with percent sand. Abundances
of Tharyx multifilis were positively correlated only with percent clay,
and were negatively correlated with percent sand.
It is apparent from these data (Figure 3.43, Table 3.23) that sediment
grain size characteristics (or other factors with which these characteristics
are highly correlated) are major determinants of benthic community structure.
The importance of these factors relative to organic enrichment and the
distribution of toxic substances in the sediments is difficult to demonstrate
conclusively because sediment grain size characteristics vary considerably
between the waterways and adjacent shoreline areas. Throughout the entire
study area, the abundances of major taxa and dominant species appear to
best reflect changes in grain size. But within each study area, the degree
3.106
-------
PERCENT TOTAL
VOLATILE SOLIDS
COMMENCEMENT
BAY
CITY
WATERWAY
Geographic distribution of sediment volatile
solids content. (Note: total volatile solids
boundaries are uncertain.)
-------
8
RUSTON
U>
O
00
COMMENCEMENT
BAY
4000
' I FEET
TACOMA
METERS
1000
PERCENT TOTAL
VOLATILE SOLIDS
1
2
3
4
5
6
7
8
LESS THAN 2
2-4
4-6
6-8
8-10
10-12
12-14
OVER 14
Figure 3.36. (Continued)
-------
u>
o
UD
13-
12 •
11-
10-
9-
O 8-
h- 7-
6-
5-
4-
3-
2-
1 -
LU
O
cc
111
o.
••
2,000 4,000 6,000 8,000 10,000 12,000 14,000
DISTANCE FROM MOUTH OF WATERWAY (FEET)
16,000
Figure 3.37. Total organic carbon content of the sediments in Hylebos Waterway.
-------
o
Ul
o
cc
LU
0.
2.3 •
2.2-
2.1 -
2 -
1.9 -
1.8-
1.7-
1.6-
1.5 -
1.4 -
1.3 -
1.2-
1.1-
1-
0.9-
0.8-
0.7-
0.6-
0.5-
0.4-
0.3-
0.2
2,000 4,000 6,000 8,000 10,000
DISTANCE FROM MOUTH OF WATERWAY (FEET)
12,000
Figure 3.38. Total organic carbon content of the sediments in Blair Waterway.
-------
8-
7 •
6 •
O
P 5-
H
UJ
OC 4 •
lit
Q.
3 -
2-
•!
•
•
•
•
• •
•
•
•
•
»
1,000 3,000 5,000 7,000
DISTANCE FROM MOUTH OF WATERWAY (FEET)
Figure 3.39. Total organic carbon content of the sediments in City Waterway.
-------
zire
TI
to
c
-s
fO
CO
-£»
0
<< o>
— ' -S
(T> O
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to
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to
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PERCENT FINES
_»ioo>^tno>^a) 8 ~
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9
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,
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-------
100
90 •
80-
W 70-
UJ
5 60-
UJ
O
cc
111
CL 50 H
40-
30 -
20
2,000 4,000 6,000 8,000 10,000
DISTANCE FROM MOUTH OF WATERWAY (FEET)
12,000
Figure 3.41. Percent fine-grained materials (silt plus clay) in the sediments of
Blair Waterway.
-------
90 1
80
70-
CO
HI
2 60
LL
I-
2
111
8 50
HI
CL
40-
30-
20
1,000
3,000 5,000
DISTANCE FROM MOUTH OF WATERWAY (FEET)
7,000
Figure 3.42. Percent fine-grained materials (silt plus clay) in the sediments of
City Waterway.
-------
15,000 -|
10,000 -
5,000 -
5,000 -
TOTAL BENTHOS
r, « 0.83**
OJ u 1 I 1 1 1 1 1 1 1 1
(n
13 10,000-1
Q
Q
Z
LL 5,000 -
O
NUMBER
o
10,000 -
-
POLYCHAETES *
rs = 0.90**
• A
V
• •
•
• »
MOLLUSCS
r, = 0.85**
20 40 60 80
PERCENT SILT AND CLAY
100
Figure 3.43.
Correlations of numerical abundances of all benthic
infauna, polychaetous annelids, and molluscs vs. the
percent of fine-grained materials (silt plus clay)
in the sediments (** = P<0.01).
3.115
-------
TABLE 3.23. RESULTS OF PEARSON PRODUCT-MOMENT CORRELATION ANALYSES
BETWEEN SEDIMENT CHARACTERISTICS, AND ABUNDANCES OF MAJOR TAXONOMIC
GROUPS AND NUMERICALLY DOMINANT TAXA (RUSTON-PT. DEFIANCE SHORELINE
AND CARR INLET STUDY AREAS DELETED)
Taxonomic Group
or Taxon
Polychaete abundance
Mollusc abundance
Oligochaete abundance
Amphipod abundance
Pric>noj£io spp.
Lumbrineris spp.
Tharyx multifilis
Axinopsida serricata
Macoma carlottensis
% TOCa
ns
ns
ns
ns
+*
ns
ns
ns
ns
Sediment
% Sand
.*
_*
+*
+**
ns
_**
_**
_*
_*
Variable
% Silt
+**
+**
_*
_**
ns
+**
ns
+**
+*
% Clay
ns
ns
ns
_**
ns
+*
+*
ns
ns
a TOC = Total organic carbon.
b ns - Not significant at an experimentwise error rate of P<0.05 (i.e.,
an error rate of P<0.0125 for each test).
c * = P<0.125; ** = P<0.0025; + = positive correlation; - = negative cor-
relation.
3.116
-------
of organic enrichment appears to explain better much of the variation in
community structure and abundance.
Data from Blair, Hylebos, and City Waterways illustrate this point
well. The proportions of fine-grained sediments (silt plus clay) exhibited
large fluctuations (more than 60 percentage points) along the lengths of
all three waterways (Figures 3.40, 3.41, 3.42). The proportions of total
organic carbon in the sediments also varied considerably in Hylebos and
City Waterways, but not in Blair Waterway (Figures 3.37, 3.38, 3.39).
Total organic carbon ranged from 3.1 to 12.2 percent in Hylebos Waterway
and from 1.2 to 8.9 percent in City Waterway, but only from 0.6 to 2.2
percent in Blair Waterway.
If grain size were the most important determinant of benthic community
structure within each of the waterways, dramatic changes in community structure
would have been evident along the lengths of all three waterways. However,
as discussed earlier, benthic community structure was very similar along
the length of Blair Waterway (Figure 3.30). Abundances of the dominant
species changed, but species composition did not. In Hylebos and City
Waterways, species composition and numerical abundances changed greatly
(Figures 3.29, 3.30), and in a pattern consistent with gradients of organic
enrichment of sediments, wherein values decreased from the heads to the
mouths of the waterways (see earlier discussion). Thus, organic content
of the sediments appeared to account for a considerable amount of faunal
variation within many of the waterways. Among the waterways, however,
changes in sediment grain size appeared to be the major determinant of
benthic community structure.
3.2.7 Indices for Decision Criteria
3.2.7.1 Introduction--
To develop indices of benthic degradation for use as decision criteria,
abundances of major benthic invertebrate taxa at potentially impacted sites
were compared statistically with their respective abundances at reference
sites. A statistically significant decrease (P<0.05) in the abundance
of an indicator taxon was considered a benthic impact (i.e., a benthic
depression). At each station, indicies were based on the abundance of
the total assemblage (i.e., total taxa) and on the abundances of polychaetes,
molluscs, and crustaceans. As a group, polychaetes, molluscs, and crustaceans
accounted for approximately 91 percent of the individuals sampled at the
48 study sites throughout Commencement Bay and Carr Inlet in March, 1984.
Echinoderms and other miscellaneous taxa were not included as indices because
they were rarely encountered during the study.
3.2.7.2 Reference Site Selection--
Sediment characteristics at Carr Inlet stations were similar to those
at stations along the Ruston-Pt. Defiance shoreline, but were considerably
different from those at most stations in the Commencement Bay waterways.
For example, percent fine-grained sediments (silt and clay) in Carr Inlet
and the Ruston-Pt. Defiance Shoreline exhibited ranges of 4-23 and 3-33
percent, respectively. By contrast, percent fine-grained sediments at
all Commencement Bay waterway stations except Station HY-44 (6 percent)
3.117
-------
ranged from 26 to 89 percent. Because abundances of total assemblages,
polychaetes, and molluscs were positively correlated (P<0.05) with percent
fine-grained sediments (see Figure 3.43, Section 3.2.6), sediment character
was a confounding variable for evaluating contaminant effects. That is,
differences between benthic assemblages in Carr Inlet and assemblages at
Commencement Bay waterway stations muddier than Carr Inlet stations could
result from either contamination or differences in sediment character.
Benthic assemblages in Carr Inlet were therefore considered acceptable
reference conditions for stations along the Ruston-Pt. Defiance shoreline,
but inadequate as reference conditions for all Commencement Bay waterway
stations except Station HY-44.
Because Carr Inlet could not be used as a valid reference area for
Commencement Bay waterway stations, Blair Waterway was substituted as a
best estimate of unimpacted waterway conditions. This waterway was selected
because 1) it was the least contaminated chemically of the seven waterways
(Section 3.1); 2) only one significant bioassay result (i.e., amphipod
mortality at Station BL-25) was found out of the twelve tested (i.e., amphipod
mortality and oyster larvae abnormality at six stations) in March, 1984
(Section 3.3); and 3) percent fine-grained sediment at Blair Waterway stations
spanned a range ( 37-84 percent) similar to that observed for all waterway
stations except Station HY-44 (26-89 percent). Thus, all Blair Waterway
stations except Station BL-25 exhibited relatively low chemical contamination,
no toxicity, and sediment characteristics similar to those found throughout
the other waterways.
To help remove the confounding effects of sediment character, Blair
Waterway stations were divided into three groups representing different
ranges of sediment characteristics. Station BL-25 was not used in this
analysis because a toxic response (amphipod mortality) was found at that
site. Reference conditions with which potentially affected stations were
compared are presented in Table 3.24. Note that Station HY-44 was compared
with Carr Inlet sites.
3.2.7.3 Statistical Comparisons--
Log- transformed abundances of total assemblages, polychaetes, molluscs,
and crustaceans were compared between potentially impacted and reference
sites using the t-test. Before each t-test was conducted, an Fma){ test
was used to test for equality of variances. For comparisons in which variances
were not equal (P<0.05), an approximate t-test (Sokal and Rohlf 1969) was
used to compare mean values.
Comparisons of the four major taxa at the 39 potentially impacted
stations sampled in Commencement Bay in March, 1984 are summarized in Table
3.25. A benthic invertebrate taxon was considered numerically depressed
if its mean abundance at a potentially impacted station was statistically
significantly lower (P<0.05) than its mean abundance at the appropriate
reference station(s) (see Table SB30), or if it was absent from the potentially
impacted site. For the two stations at which a major taxon was absent
(SP-14 and RS-18), a t-test could not be conducted because the variances
equalled zero. However, if even a single individual had been captured,
the mean abundance would have differed significantly (P<0.05) from reference
3.118
-------
TABLE 3.24. PAIRINGS OF REFERENCE STATIONS AND POTENTIALLY IMPACTED
STATIONS USED FOR STATISTICAL COMPARISONS
Reference Range of Potentially Range of
Station(s) % Finesa Impacted Stations % Fines9
BL-28 37 SP-11, SP-12, SP-15 26-49
CI-11, CI-22
HY-14
BL-11 55-64 SP-14, SP-16, 55-80
CI-13, CI-16, CI-17,
CI-20
HY-12, HY-17,
HY-22, HY-28, HY-32,
HY-37, HY-42, HY-43,
HY-47
SI-11, SI-12
MD-12
BL-13 84
CR-11 4-23
CR-12
CR-13
CR-14
HY-23,
SI-15
MI-11,
BL-25
RS-12,
RS-18,
HY-44
HY-24,
MI-13,
RS-13,
RS-19,
HY-50
MI-15
RS-14
RS-20
81-89
3-33
a
Silt and clay.
3.119
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TABLE 3.25. COMPARISONS OF MEAN ABUNDANCES OF BENTHIC INVERTEBRATE
TAXA BETWEEN POTENTIALLY IMPACTED STATIONS AND REFERENCE STATIONS2
Potentially Impacted Taxon Total
Station Total Polychaeta Mollusca Crustacea Depressions
HY-12 0
HY-14 * 1
HY-17 * * 2
HY-22 * * 2
HY-23 *b * * 3
HY-24 0
HY-28 0
HY-32 * * * 3
HY-37 * 1
HY-42 0
HY-43 0
HY-44 0
HY-47 * 1
HY-50 0
BL-25 0
SI-11 * 1
SI-12 * 1
SI-15 0
MI-11 °
MI-13 °
MI-15 0
SP-11 0
SP-12 0
SP-14 * DC * * 4
SP-15 * * 2
SP-16 * 1
MD-12 0
CI-11 * 1
CI-13 * * * * 4
CI-16 * * * * 4
CI-17 0
CI-20 0
CI-22 0
RS-12 0
RS-13 0
RS-14 0
RS-18 * 0 0 * 4
RS-19 * 1
RS-20 * 1
a Reference stations are listed in Table 3.24.
b An asterisk denotes that mean abundance of a major taxon at a potentially impacted station
was significantly lower (P<0.05, experimentwise) than mean abundance at the reference station(s)
(i.e., a benthic depression).
c 0 = A major taxon was absent from a potentially impacted station (i.e., a benthic depression).
3.120
-------
conditions. Therefore, absence of a major taxon was considered as severe
as a significantly depressed (P<0.05) abundance.
No benthic depressions were found at stations in Middle and Milwaukee
Waterways. In Sitcum Waterway, single depressions (Crustacea) were found
at two of the three stations (SI-11 and SI-12). The remaining four study
areas (Hylebos, St. Paul and City Waterways, and the Ruston-Pt. Defiance
Shoreline) included stations with multiple benthic depressions.
In Hylebos Waterway, a cluster of stations (HY-17, HY-22, and HY-23)
with multiple benthic depressions was found near the head of the waterway.
In addition, a single station (HY-32) with multiple depressions was found
farther down the waterway.
In St. Paul Waterway, multiple benthic depressions were found at the
two stations (SP-14 and SP-15) located closest to the Champion International
paper mill. Polychaetes were absent from the station located closest to
the mill (SP-14). In addition, the number of depressions per station showed
a decreasing gradient with distance from the mill. No depressions were
found at stations located within the waterway proper.
In City Waterway, stations with multiple depressions were found near
the head of the waterway (CI-13) and in the Wheeler Osgood branch (CI-16).
No benthic depressions were found at the mouth of the waterway.
Along the Ruston-Pt. Defiance Shoreline, multiple benthic depressions
were found only at the station located closest to ASARCO (RS-18). Two
taxa (Polycheata and Mollusca) were absent from that station. No benthic
depressions were found at any of the three stations located southeast of
ASARCO (RS-12, RS-13, and RS-14).
Of the invertebrate taxa used as indices in the foregoing analysis,
Mollusca was the most sensitive indicator of benthic impacts, with 15 of
the 39 stations showing depressed abundances of this taxon. Crustacea
ranked second relative to impact sensitivity, with depressions at 10 stations.
Finally, total taxa and Polychaeta were the least sensitive indicators
of impacts, with depressions found at only seven and five stations,
respectively.
3.2.8 Comparisons with Past Studies
The only benthic infaunal sampling undertaken along the Ruston-Pt. Defiance
Shoreline or in the Commencement Bay Waterways that is capable of providing
data for long-term comparisons was conducted by Orlob et al. (1950) during
the summer of 1950. The utility of those data for comparisons with present
conditions is severely limited for several reasons. First, the size of
the sampler was not stated and replicates were apparently not collected
at each station. Second, although samples were washed on screens, the
mesh size was not stated. Third, only some of the organisms in the samples
were retained for identification. These limitations preclude quantitative
comparisons with present biological conditions. However, some of the quali-
tative observations made by Orlob et al. (1950) are informative.
3.121
-------
In general, Orlob et a!. (1950) collected reasonably diverse assemblages
of benthic organisms along most of the Ruston-Pt. Defiance Shoreline, with
the exception of the area near ASARCO (Station RS-18 from the present study).
No living benthic organisms were collected there in 1950 and only very
low numbers of benthic organisms were collected during the present study.
Reasonably diverse assemblages were also collected at the mouths of major
waterways. However, sampling along the lengths of the Hylebos and City
Waterways failed to collect any benthic macroinvertebrates in the upper
reaches of either waterway. Orlob et al. (1950) attributed the apparent
lack of benthic organisms in the upper Hylebos Waterway to "domestic sewage
and industrial wastes from various plants, including two large chemical
firms." The lack of benthic invertebrates in the upper City Waterway was
attributed to wastes from a meat packing plant. Sediments in this area
exuded a strong odor of hydrogen sulfide, which is consistent with extreme
organic enrichment.
Although conditions in the vicinity of Station RS-18 do not appear
to have improved during the 34-yr interval, some improvement in upper Hylebos
and City Waterways seems to have occurred, as these areas are no longer
devoid of benthic life. However, due to the very sketchy nature of the
data collected by Orlob et al. (1950), no other conclusions regarding temporal
changes are appropriate.
3.2.9 Summary
• Benthic assemblages in the Commencement Bay waterways are
distinct from assemblages in Carr Inlet and the Ruston-Pt.
Defiance Shoreline, as evidenced by reduced numbers of species,
high dominance, and enhanced total abundances within the
waterways
t Overall benthic community characteristics in the waterways
are indicative of environmental stress that may be associated
with toxic contamination, sediment disturbance, or physical
characteristics (e.g., grain size) of the sediments. However,
the overall high abundances of a mixed polychaete-mollusc
assemblage indicate that any broad-scale stresses are not
sever.
• A characteristic Th aryx-Ax i nops ida assemblage occurred throughout
much of the waterway area, including Blair, Sitcum, and
Milwaukee Waterways, the mouth of City Waterway, and the
mouth of Hylebos Waterway.
• Within many of the waterways, organic content of the sediments
appears to account for a considerable amount of faunal
variation. Among the waterways, changes in sediment grain
size appear to be the major determinant of benthic community
structure.
• Excessive organic enrichment of sediments appears to have
been occuring at some stations where nematodes and the polychaete
Capitella capitata exhibited very high abundances (relative
3.122
-------
to the Tharyx-Axi nops i da community and communities in the
control area), and comprised most of the organisms collected.
• Stresses other than those resulting from organic enrichment
appear to have been occurring at a few stations in the waterways
and along the Ruston-Pt. Defiance Shoreline where total
abundances were very depressed (relative to the Tharyx-Axinopsida
community and communities in the control area).
• Abundances of major benthic invertebrate taxa (i.e., total
abundance, Polychaeta, Mollusca, and Crustacea) were not
depressed significantly (P<0.05) at any station in Middle
or Milwaukee Waterways. In Sitcum Waterway, single depressions
(Crustacea) were found at two of three stations.
• Multiple benthic depressions were found in Hylebos, St. Paul,
and City Waterways, and along the Ruston-Pt. Defiance Shoreline.
Areas having multiple depressions included the head of Hylebos
Waterway (HY-17, HY-22, and HY-23), the middle of Hylebos
Waterway (HY-32), the stations closest to Champion International
(SP-14 and SP-15), the head of City Waterway (CI-13), the
Wheeler Osgood branch of City Waterway (CI-16), and the
station closest to ASARCO (RS-18).
• Spatial patterns of benthic depressions are presented in
Figure 3.44.
t Benthic biological conditions do not appear to have improved
in the vicinity of Station RS-18 since it was first sampled
in 1950. Some improvement does appear to have occurred
at the head of Hylebos and City Waterways during this time
interval.
3.3 SEDIMENT TOXICITY
3.3.1 Introduction
Sediment toxicity tests were conducted as part of the Commencement
Bay Investigations to determine if laboratory exposures of the sediments
were acutely toxic to representative organisms. The degree of sediment
toxicity was used in the decision-making approach as one of the indicators
to identify and prioritize problem areas.
Two separate test procedures were conducted on each sediment sample:
the amphipod mortality bioassay and the oyster larvae abnormality bioassay.
The amphipod bioassay was used to measure a direct lethal response. Partial
life-cycle tests with oyster larvae were used to measure the induction
of abnormal development in developing embryos after a 48-h exposure to
sediments. Significant oyster larvae abnormalities compared to controls
are indicative of chemical toxicity (Cardwell et al. 1979; Chapman and
Morgan 1983). Data on the relative survival of exposed oyster larvae were
also collected to aid in the interpretation of abnormality data.
3.123
-------
NO DEPRESSION
1 DEPRESSION
> 1 DEPRESSION
COMMENCEMENT
BAY
ro
COMMENCEMENT
BW
CITY
WATERWAY
Figure 3.44. Summary of spatial patterns of benthic depres-
sions.
-------
The bioassays were conducted on intact sediment samples (i.e., non-
dilution tests) and on sediment samples diluted with clean (i.e., reference)
sediments (i.e., dilution bioassays).
3.3.2 Amphipod Sediment Bioassays
3.3.2.1 Non-Dilution Bioassays--
Results of the non-dilution amphipod bioassay tests are summarized
in Table 3.26. Clean sediment control mortality values ranged from 4 to
10 percent; a mean mortality of 10 percent is considered acceptable for
amphipod sediment bioassay controls (Swartz et al. 1985). Mortality in
Cd-spiked sediments was 94 percent, which is consistent with the expected
mortality rate.
ANOVA indicated no significant difference (P>0.05) in mean mortality
values among the clean sediment controls. Results for Commencement Bay
sediments were compared with those for the reference area (Carr Inlet)
using the t-test. One reference sediment sample had an exceptionally high
amphipod mortality (CR-11; mean mortality = 25 percent), that was significantly
higher than mortalities in the other three reference samples. The overall
low survival resulted from a high mortality in only one of the five replicates
at this station. Consequently, this sample was deleted from the statistical
comparisons. The subsequent analysis indicated that mortalities in 18
test sediments were significantly different (P<0.05, experimentwise error
rate) from the Carr Inlet samples.
3.3.2.2 Dilution Bioassays--
Results of the amphipod sediment dilution bioassays are summarized
in Table 3.27. Results indicate that for five of the six sediments tested,
a 25 to 50 percent concentration of test sediment (i.e., a 50 to 75 percent
dilution) was sufficient to eliminate the toxic response. The only exception
was combined sediment from Stations RS-18 and RS-19, which was still highly
toxic at the lowest test sediment concentration (10 percent) assayed.
Comparison of the initial (non-dilution) bioassays on these sediments
with results of the 100 percent test sediment concentration for the dilution
bioassays indicated a high level of agreement (Table 3.28). Ihe only exception
was sediment from Station CI-11, which initially gave a mean mortality
of 52.0 percent, and subsequently gave a mean value of 25.0 percent. This
difference is most probably due to a reduction in toxicity with storage,
a phenomenon documented by Cummins (Cummins, J., January, 1983-February, 1984,
personal communication). Test sediments used for dilution bioassays were
stored for approximately 1 mo after collection.
3.3.3 Oj/ster Larvae Sediment Bioassays
3.3.3.1 Non-Dilution Bioassays--
Results of the non-dilution oyster larvae bioassay tests are summarized
in Table 3.29. In addition to larval numbers, oyster embryo response is
expressed in terms of mean percent abnormal larvae and mean percent mortality
(compared to clean seawater controls). Salinity, pH, and dissolved oxygen
3.125
-------
TABLE 3.26. SUMMARY OF NON-DILUTION AMPHIPOD BIOASSAY RESULTS
Station
HY-12
HY-14
HY-17
HY-22
HY-23
HY-24
HY-28
HY-32
HY-37
HY-42
HY-43
HY-44
HY-47
HY-50
B-03
B-04
B-19
B-10
BL-11
B-12
BL-13
B-15
BL-21
BL-25
BL-28
BL-31
SI-11
SI-12
SI-15
MI-11
MI-13
MI-15
SP-11
SP-12
SP-14
SP-15
SP-16
MD-12
Percent
Mortal ity»
16
9
19
36*
26*
19
8
20
18
37*
19
15
25
16
16
13
19
20
13
20
19
27*
14
28*
8
16
24
31*
25*
24*
14
20*
12
16 K
100*b
68*
27*
13
Station
CI-11
CI-13
CI-16
CI-17
CI-20
CI-22
RS-12
RS-13
RS-14
RS-18
RS-19
RS-20
RS-22
RS-24
CR-11
CR-12
CR-13
CR-14
Controls
Clean
Sediment
a
b
c
d
e
f
g
y
Cd-Spiked
Sediment
Percent
Mortality9
52*
20
14
17
30*
19
15
32*
20
95*
77*
5
10
28*
25
11
7
10
4
7
g
Q
4
10
8
9
94
8 Percent mortality is based on five replicate samples per station. Asterisk
denotes that mean mortality was significantly different (P<0.05 experimentwise)
from the mean mortality of pooled replicates from CR-12, CR-13, and CR-14
(i.e., 9.3 percent, n«15).
b Because 100 percent mortality occurred for all five replicates at SP-1«,
no variance about the mean existed and a t-test could not be conducted.
However, the observed level of mortality was considered at least as severe
as the levels determined to be significant (P<0.05) at other sites.
3.126
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TABLE 3.27. SUMMARY OF AMPHIPOD SEDIMENT DILUTION BIOASSAYS
Station Test Sediment
Number Concentration3
HY-22
HY-22
HY-22
HY-22
HY-22
HY-22
HY-42
HY-42
HY-42
HY-42
HY-42
HY-42
BL-25C
BL-25
BL-25
BL-25
BL-25
BL-25
SP-14
SP-14
SP-14
SP-14
SP-14
SP-14
CI-11
CI-11
CI-11
CI-11
CI-11
CI-11
RS-18/19c'e
RS-18/19
RS-18/19
RS-18/19
RS-18/19
RS-18/19
100
75
50
25
10
0
100
75
50
25
10
0
100
75
50
25
10
0
100
75
50
25
10
0
100
75
50
25
10
0
100
75
50
25
10
0
Percent Mortality
Nb Mean SD
5
5
5
5
5
5
5
5
5
5
5
5
NDd
1
2
3
2
3
4
4
4
4
4
4
5
5
5
5
5
5
ND
2
2
3
3
3
31.0
26.0
25.0
18.0
20.0
10.0
35.0
27.0
26.0
9.0
7.0
3.0
ND
25.0
7.5
10.0
12.5
10.0
100.0
100.0
97.5
21.0
18.5
8.5
25.0
21.0
13.0
25.0
17.0
7.0
ND
100.0
90.0
98.5
55.0
8.5
2.6
2.8
2.3
1.8
2.0
2.0
2.4
0.9
2.4
1.8
1.7
0.9
ND
N/A
0.7
1.0
0.7
1.0
0
0
0.6
2.9
1.9
0.5
2.5
1.8
2.3
2.6
2.3
0.9
ND
0
1.4
0.6
2.6
1.2
a Percent of test sediments mixed with West Beach control sediments.
The 0-percent concentration contains only control sediments
Number of replicate bioassays conducted at each sediment dilution.
Each replicate bioassay was performed with 20 amphipods.
c Insufficient sediments for these samples for five replicate
at each sediment concentration.
d ND = No data.
e Samples RS-18 and RS-19 were combined due to a lack of sediments.
3.127
-------
TABLE 3.28. COMPARISONS OF INITIAL AND DILUTION BIOASSAYS FOR
AMPHIPOD MORTALITY AND OYSTER LARVAL ABNORMALITY
Percent Amphipod Mortality Percent
a Assay
b un - r
Station
HY-22
HY-42
BL-25
SP-14
CI-11
RS-18/19
Seawater Control
Sediment Control
response to 100-percent
* r\ H a^ a
Initial Di
36.0
37.0
28.0
100.0
52.0
86 .Od
NAe
NA
test sediments
Oyster Abnormality
lution3 Initial
31.0
35.0
NDb
100.0
25.0
ND
NA
NA
(i .e., 0-percent
39.0
29.2
19.9
100 .Oc
63.0
58.1
4.1
10.1
control
Dilution3
ND
33.8
35.3
100. Oc
40.6
62.3
6.9
8.1
sediments) .
c Nominally 100 percent abnormality since there was 100 percent mortality.
d Mean of RS-18 and RS-19 bioassay results.
g
NA = not applicable.
3.128
-------
TABLE 3.29. SUMMARY OF NON-DILUTION OYSTER LARVAE BIOASSAY RESULTS
Station
HY-12
HY-14
HY-17
HY-22
HY-23
HY-24
HY-28
HY-32
HY-37
HY-42
HY-43
HY-44
HY-47
HY-50
B-03
B-04
B-09
B-10
BL-11
B-12
BL-13
B-15
BL-21
BL-25
BL-28
BL-31
SI-11
SI-12
SI-15
MI-11
MI-13
MI-15
SP-11
SP-12
SP-14
SP-15
SP-16
MD-12
Mean Number
of Larvae3
40
148
75
62
70
173
109
124
117
89
167
146
110
129
55
36
47
25
230
31
115
35
157
128
165
178
203
179
156
182
147
165
163
122
1
54
64
136
Percent Relative
Mortality13
46
64
82
85
83
58
73
70
71
78
59
64
73
69
40
61
49
73
44
66
72
62
62
69
60
57
51
56
62
56
64
60
60
70
99
87
84
67
Percent
Abnormal ityc
45.6*
25.4
41.0*
39.0*
35.5*
24.7
22.8
23.8
22.5
29.2
21.3
15.5
32.4*
26.4
13.4
24.3
20.2
30.2
17.5
17.8
21.0
26.1
22.9
19.9
15.9
18.1
16.0
18.1
16.2
22.6
16.1
16.8
20.7
29.9*
100.0*
61.9*
36.0*
23.7
3.129
-------
TABLE 3.29. (Continued)
CI-11 85 79 63.0*
CI-13 77 81 31.9*
CI-16 78 81 32.2*
CI-17 148 64 22.0
CI-20 70 83 31.6*
CI-22 179 56 20.3
RS-12 152 63 21.9
RS-13 111 73 30.1
RS-14 178 57 18.1
RS-18 37 91 69.6*
RS-19 97 76 46.5*
RS-20 240 42 8.6
RS-22 256 38 8.5
RS-24 146 64 21.3
CR-11 175 57 16.8
CR-12 203 51 11.3
CR-13 191 53 9.9
CR-14 180 56 14.3
Seawater
control 411 - 4.1
Sediment
control 313 24 10.1
a Numerals are the mean numbers of larvae used to determine abnormalities.
Means are based on duplicate tests for all field stations and on five tests
for the seawater and sediment controls.
b Percent of larvae that died before test was terminated, in terms of the
mean seawater control mortality which was assigned a value of 0 percent.
c Percent of larvae showing developmental abnormalities. Asterisks denote
values significantly different (P<0.05 experimentwise) from that observed
in Carr Inlet (i.e., CR-11, CR-12, CR-13, and CR-14 pooled).
3.130
-------
remained at acceptable levels [as defined by ASTM (1983): pH range 7.3-8.3;
salinity range 20-35 ppt; dissolved oxygen range 4-12 mg/L] in most test
containers, including those eliciting adverse larval response (pH range
7.3-8.0; salinity range 27.5-28.5; dissolved oxygen range 4.0-7.8 mg/L).
The only exceptions were samples from Stations RS-18, SP-14, SP-15, HY-12,
HY-17, and CI-11, which had dissolved oxygen values below 4 mg/L at termination.
Seawater controls had a mean abnormality rate of 4 percent, which
is well below the 10 percent abnormal development criterion suggested by
ASTM (1983) as acceptable for bivalve larvae bioassay controls. Mean
mortality in the Cd-spiked seawater was 100 percent, and mean mortality
in the Cd-spiked sediment was >99 percent. These results are in agreement
with expected mortality rates for the spiked samples.
Mortality values generally agreed with data on abnormalities. At
stations with mean abnormalities of <20 percent, mortality rates were generally
low (i.e., <30 percent).
Results for Commencement Bay stations were compared with those for
the reference area (Carr Inlet) using the t-test. The analysis indicated
that the mean abnormalities in 15 test sediments were significantly different
(P<0.05, experimentwise error rate) from those in the Carr Inlet samples.
Sediment samples displaying significantly increased oyster larvae abnormality
rates are identified in Table 3.29.
3.3.3.2 Dilution Bioassays--
Results of the oyster larvae sediment dilution bioassays are summarized
in Table 3.30. Salinity, pH, and dissolved oxygen values remained at acceptable
levels [as defined by ASTM (1983)] for samples from Stations HY-42, RS-18/19,
and BL-25. However, dissolved oxygen levels for samples from Stations
CI-11 and SP-14 were below 4 mg/L in all but the 90 percent dilutions with
clean material. This depression in dissolved oxygen concentration was
probably caused by the high organic content of these sediments (9 and 16
ppm TOC, respectively).
Results indicate that oyster abnormality decreases with declining
concentrations of test sediments that were progessively diluted with clean
control sediments. In test sediments from Stations HY-42 and BL-25, dilutions
of 75-90 percent were required to reduce oyster abnormality to control
levels. For samples from Stations SP-14, CI-11, and RS-18/19, dilutions
greater than 90 percent were required to reduce sediment toxicity to control
levels. Calculation of 48-h EC™ values indicated that the most toxic
sediments were those from Stations RS-18/19 (ECso = 9.8 g/L) and SP-14
(EC5Q =6.8 g/L). However, it should be noted that both of these sediments
were high in organic matter, as well as being high in contaminant concentra-
tions.
Comparison of the initial (non-dilution) bioassays on these sediments
with the results of the 100 percent test sediment concentration for the
dilution bioassays indicated a high level of agreement for three of five
sediments: HY-41, SP-14, and RS-18/19 (Table 3.28). Sediments from Station
BL-25 showed an increase in toxicity and those from Station CI-11 showed
a decrease in toxicity, which may be attributable to the effects of sediment
3.131
-------
TABLE 3.30. SUMMARY OF OYSTER LARVAE SEDIMENT DILUTION BIOASSAYS
Relative
Percent Mortality0
Station Test Sediment Number
Number Concentration3 Surviving"
HY-42
HY-42
HY-42
HY-42
HY-42
BL-25
BL-25
BL-25
BL-25
BL-25
SP-14
SP-14
SP-14
SP-14
SP-14
CI-11
CI-11
CI-11
CI-11
CI-11
RS-18/19
RS-18/19
RS-18/19
RS-18/19
RS-18/19
Seawater Control
Sediment Control
100
75
50
25
10
100
75
50
25
10
100
75
50
25
10
100
75
50
25
10
100
75
50
25
10
0
0
49
81
48
161
160
58
46
121
154
191
0
2
10
19
51
66
25
58
72
103
25
38
49
16
123
286
200
Mean
83.0
71.7
83.2
43.9
44.1
79.9
84.1
57.7
46.2
33.4
100.0
99.5
96.7
93.4
82.3
76.9
91.4
79.7
75.0
64.0
91.3
86.9
82.9
94.6
57.0
— —
30.1
SO
2.2
4.0
11.4
9.6
13.4
9.6
5.2
8.9
23.2
21.0
0
0.7
1.2
2.0
4.2
5.9
2.7
8.9
6.2
6.9
3.0
5.2
3.0
4.2
4.5
— _
5.4
Percent Abnormality'*
Mean
33.8
31.5
30.8
17.8
1.4
35.3
32.7
21.4
21.6
11.4
_.
66.7
84.5
36.2
24.0
40.6
41.1
37.8
40.0
25.0
62.3
62.8
50.4
55.7
25.0
6.9
8.1
SO
2.8
0
1.7
0.9
2.0
2.1
1.8
1.3
5.2
2.1
^_
0
1.7
4.1
6.9
2.4
1.5
3.2
1.0
7.5
1.3
0.4
4.4
2.1
5.4
0.4
1.3
a Percent of test sediments mixed with West Beach control sediments.
The 0-percent concentration contained only control sediments.
b Mean of two replicates after 48-h exposure to sediments.
Percent mortality relative to the mean number of surviviny embryos
and larvae in the seawater control.
° Percent of surviving embryos and larvae that had not developed to
straight-hinye stage.
3.132
-------
storage (Cummins, J., January, 1983-February, 1984, personal communication).
3.3.4 Discussion
3.3.4.1 Amphipod Bioassays--
The use of Rhepoxynius abronius to determine the acute lethality of
field-collected sediments has been documented by Swartz et al. (1982a,
1985), Chapman et al. (1982a,b), and Chapman and Fink (1984). This amphipod
species is a sensitive indicator of contaminated areas both by its absence
from some natural populations in such areas (Swartz et al. 1982a; Comiskey
et al. 1984), and by its response to contaminated sediments in laboratory
studies (Swartz et al. 1985).
In the present study, exposure to sediments from 18 stations of the
52 induced statistically significant acute lethality to !?. abronius as
compared to a reference area (Carr Inlet). All areas tested, with the
exception of Middle Waterway (one station), contained one or more sampling
sites with statistically significant amphipod mortality.
During the amphipod bioassays, sediment sample SP-14 from the area
of Champion International developed a white, gelatinous mass on the sediment
surface. This mass was determined by microscopic examination to be inhabited
by filamentous, colorless bacteria, which were probably sulfur bacteria.
Their appearance on the sediment surface indicated that the sediments were
anoxic through to the surface. Vigorous aeration failed to oxygenate these
exposures. The amphipods more likely died from anoxia in this sample than
from other causes. Low dissolved oxygen was not a problem in any other
amphipod bioassay.
3.3.4.2 Oyster Larvae Bioassays--
In the present study, exposure to sediments from 15 of the 52 stations
induced statistically significant oyster larvae abnormalities as compared
to the reference area (Carr Inlet). Exposure to sediments from four of
the eight areas in Commencement Bay tested induced significantly increased
oyster larvae abnormalities: Ruston-Pt. Defiance Shoreline, St. Paul Waterway,
City Waterway, Hylebos Waterway.
Water quality data taken after the 48-h bioassay period indicated
that high larval mortality and high abnormality rates from exposure to
sediments from 5 of the 50 tested stations were at least partly attributable
to low dissolved oxygen levels (3-4 mg/L at termination): Stations SP-14,
SP-15, HY-12, HY-17, and CI-11. The very low dissolved oxygen concentrations
at Station RS-18 (<1 mg/L) may be responsible for the bioassay toxicity
observed. All of these stations had organically enriched sediments with
TOC concentrations exceeding 5 ppm.
In cases of low dissolved oxygen during bioassay exposures, it is
not possible to discriminate between potential effects of lack of oxygen
and toxic chemical contamination. At Station SP-14 there was evidence
of stress due to low dissolved oxygen in both the amphipod and oyster larvae
bioassays. However, at Stations HY-12 and HY-17 there were no statistically
significant amphipod mortalities, as well as no evidence of stress due
3.133
-------
to low dissolved oxygen in the amphipod exposure. Therefore, at these
sites the effects on oyster larvae may have been the result of low oxygen,
At Stations SP-15 and CI-11, there were significant amphipod mortalities
with no evidence of oxygen depletion. These results indicate the presence
of toxic contamination that may have also caused the oyster larvae abnormali-
ties.
3.3.4.3 Dilution Bioassays--
In both amphipod and oyster larvae sediment bioassays, dilution of
selected toxic sediments with clean sediments reduced toxicity. Similar
results were observed by Chapman and Fink (1984) in sediment dilution studies
measuring sublethal oligochaete respiratory response to sediments from
Elliott Bay. In the amphipod bioassays, a 50-75 percent dilution was generally
sufficient to eliminate the toxic response. Chapman and Fink (1984) found
a 50 percent dilution was sufficient to eliminate the toxic response in
oligochaete respiration bioassays. However, in the oyster larvae bioassays,
dilutions of 70-90 percent or greater were required to eliminate the toxic
response. This difference is not surprising, since the oyster larvae bioassay
is more sensitive than the amphipod or oligochaete respiration bioassay
(Chapman et al. 1984).
3.3.4.4 Comparison of Bioassays--
A comparative summary of sediment toxicity as determined by the amphipod
and oyster larvae bioassays is presented in Figures 3.45-3.47. Sediments
from 24 of the 52 stations tested were toxic in at least one of these two
tests. Similar results were obtained for 10 stations by both methods,
and approximately equal numbers of samples were toxic by only one method
(amphipod bioassay-seven samples; oyster larvae bioassay-six samples).
The level of agreement for the presence of toxic effects (10 of 23 tests
or 43 percent) between the two tests is considered to be high, considering
the two kinds of response (i.e., lethal and sublethal) and the two life-
stages (i.e., adult organism and fertilized egg). As noted by Chapman
and Long (1983), different bioassay organisms and tests will respond differently
to the same sediment sample, reflecting both their own uniqueness and that
of the sample.
The relationship between amphipod mortality and oyster larvae abnormality
for individual sampling stations is shown in Figure 3.48. Nonparametric
statistical comparisons using Spearman's rank correlation coefficient indicate
a highly significant degree of agreement between the two bioassay responses
(P<0.0001). This close association of results is also indicated by a coeffi-
cient of determination (R?) of 0.725. The slope of the regression relationship
was 1.02, indicating an almost equal agreement between the magnitudes of
the two responses.
3.3.5 Comparison with Historical Data
Previous R. abronius sediment bioassay tests in Commencement Bay have
been conducted "By Swart z et al. (1982a), who tested 175 sediment samples,
129 of which were from Commencement Bay waterways. The remaining samples
were from the outer bay. Two samples from the Ruston-Pt. Defiance Shoreline
were from different areas than those sampled in the present study. Data
3.134
-------
IZZ AMPHIPOD MORTALITY
OYSTER LARVAE ABNORMALITY
P< 0.05
CD
en
c
o
Q.
(0
CO
o:
.»-»
c
Q)
O
0)
Q.
c
0
0)
70
60
50
40
30
20
10
0
HYLEBOS WATERWAY
*
p;
\
S
S
\
S
S
\
/\
/\
/ \
/s
f— n ttf^f
f—
P
(/
-_
S
\
S
\
s
s
f7
/
/
/
/
S
s
s
s
s
\
s
s
\
s
1*
/
/
/
/
/
/
/
/
/
rq
\
s
s
s
\
\
\
\
s
#
*
•r
/
/
/
/
/
/
\
\
S
S
\
\
\
\
\
v
/
/
/
/
\
\
\
\
\
\
u
y
^
\
\
\
\
s
*
7
/
/
/
/
\
\
\
\
\
s
p-
/
/
/
/
rq
\
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\
\
\1
/
/
/
/
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__
\
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\
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r~q
7
/
/
/
/
\
\
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/
/
/
v
^
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s
\
~.
/
/
/
/
/
/
V
\
\
\
\
\
\
s
*
\
s
/ X,
/\
/\
/\
HV-12 HY-17 HY-23 HY-28 HY-37 HY-43
HY-14 HY-22 HY-24 HY-32 HY-«2 HY-M
HY-SO
3U -
40 -
30 -
20 -
10 -
n -
BLAIR WATERWAY
* *
—
/
/
/
-^
s
7
/
/
/
r/
•^
s
s
/
/
/
/
/
-^
s
s"
s
/
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-N V
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N /
\1 /
^
s
s
v~
p
y
I/
si
s
/
/
/
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Si
S
\
71
/
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"q
S
\
p
[/
\
S
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[7
/
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\
p
/
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•r
s
s
s
s
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/
/
/
/
s
s
s
\
s
s
s
BUI BL-13 B-12
BL-K 8-15 BL-28 B-09 BL-31
B-10
Figure 3.45.
Bioassay responses to sediments from Hylebos
and Blair Waterways.
3.135
-------
100 -
90 -
80 -
70 -
60 -
50 -
40 -
.
i
/ \
^
"t^ MO-13 MI-11 MH3 MI-IS SMI SM2 SMS SP-11 SP-12 SP-14 SP-1S
O3O
y \j — i
0)
Q_ 80-
C 70-
D
-^- 60 -
*£.
50 -
40 -
30 -
20 -
10 -
0_
CITY WATERWAY
*
^
* \S;
^
%$$
^%
^
// \\
^$$
s x^
y/vv
» * »«_
i i ^ ^
___ \\ v\ \\ //
; s \\v v\N v\N f/s
VVOO j , OO Vy\\> '//
11 ^ 11 %
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sv
//
y/
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-7
/
/
/
*
\
\
\
\
\
\
\
V
SP-16
i
CI-11 CI-13 CI-16 CI-17 CI-20 CI-22
Figure 3.46. Bioassay responses to sediments from Middle,
Milwaukee, Sitcum, St. Paul, and City Waterways.
3.136
-------
IZZ AM PHI POD MORTALITY
OYSTER LARVAE ABNORMALITY
P < 0.05
100
90 -
80 -
70 -
60 -
Q) 50-
i -•>
to" 3°-
o: 20-
.*-»
c ioH
RUSTON-PT. DEFIANCE
SHORELINE
V>*
#
'1,
0)
0.
C
O
0) 60
RS-12 RS-13 RS-14 RS-18 RS-19 RS-20 RS-22 RS-24-
50 -
40 -
30 -
20 -
10 -
0
CARR INLET
(REFERENCE)
CR-11
CR-12
CR-13
CR-14
Figure 3.47.
Bioassay responses to sediments from Ruston-
Pt. Defiance Shoreline and Carr Inlet.
3.137
-------
100
87.5
75
i
o
62.5
50
O
O
CL
X 37.5
n.
25
12.5
6 12 18 24 30 36 42 48 54 60 66 72 78 84 90 96 100
OYSTER LARVAE ABNORMALITY (%)
Figure 3.48.
Relationship between amphipod and oyster larvae
bioassay results.
3.138
-------
for 125 of the 129 waterway stations represent unreplicated samples. Of
the 129 waterway samples, the results for 78 (60 percent) exceeded the
highest possible control mortality, while 101 samples (78 percent) were
above the level detected by ANOVA to be statistically significant for repre-
sentative samples (Swartz, R., January 9-February 3, 1984, personal communi-
cation). By contrast, in the present study only 15 of 44 samples from
the waterways (34 percent) were significantly lethal by this test.
There are three primary reasons for the apparent differences between
the present study and previous work by Swartz et al . (1982a). First, the
use of replicated samples in the present study enabled more rigorous, statis-
tical determinations of lethality. Second, some of Swartz et al.'s (1982a)
samples were nearshore, whereas the present study collected all samples
from offshore areas. For instance, Swartz et al. (1982a) found that nearshore/
intertidal sediments near the Lincoln Avenue drain in Blair Waterway were
relatively lethal, whereas in the present study sediment tested from this
area was only collected from mid-channel (Station BL-21), and this material
was determined to be nonlethal to the amphippds. Third, there was a 3-yr
time period between the two studies, during which time sediment toxicity
may have dec!ined.
In some areas of overlap between the present study and that of Swartz
et. al. (1982a) (e.g., Stations HY-22, HY-23, HY-25, SI-15, SP-14, and
CI-11), sediments found to be particularly lethal by Swartz et al. (1982a)
were also significantly lethal in the present study. There are also areas
of overlap where relatively high mortalities were recorded by Swartz et
al. (1982a), while testing with amphipods in the present study indicated
no significant lethality. These areas include Stations HY-17, HY-32, and
CI-16. It is possible that sediment toxicity in these areas has been reduced
due to dredging, sedimentation, cessation of contaminant inputs, or other
causes. However, it is also possible that these differences between the
two studies are simply a function of the patchy distribution of sediment
toxicity in the waterways (Swartz et al. 1982a). Results of the replicate
tests conducted in the present study should be considered representative
of present conditions at the stations tested.
Oyster larvae sediment bioassay tests in Commencement Bay have also
been conducted by Chapman et al. (1983) and Pierson et al. (1983). The
latter investigators tested nine stations in Blair and Sitcum Waterways
using different techniques than in the present study. Unacceptably high
control abnormalities (range of means was 12.4 to 100 percent) negate the
usefulness of these data, and this study is not further considered herein.
Chapman et al. (1983) tested nine stations using the oyster larvae
bioassay in Commencement Bay waterways, including Hylebos, Blair, Sitcum,
and City Waterways. Results were compared using subjective, rather than
statistical, criteria. Exposure to sediments from seven of these nine
stations (78 percent) resulted in high toxicity compared to controls based
on >20 percent mean abnormalities. Mean control abnormalities were
<2 percent. In the present study, 16 of 44 stations (36 percent) were
significantly toxic based on oyster larvae abnormalities. As was the case
with the amphipod tests, there was an apparent decrease in overall toxicity
in the present study compared to previous testing. Seven of the nine stations
tested by Chapman et al. (1983) overlapped with stations in the present
3.139
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study. Results from five of these were similar in both studies (Stations
HY-14, HY-23, HY-47, SI-15, CI-22). Sediments from two of the nine common
stations (Stations BL-21, CI-17) showed relatively high toxicity in previous
studies but no significant toxicity in the present study. Whether there
has been a reduction in sediment toxicity between Chapman et al.'s (1983)
sampling in August, 1982 and the present sampling in March, 1984 cannot
be determined based on comparisons between only nine samples.
3.3.6 Summary
• Sediments from 24 of the 52 Commencement Bay sites tested
had statistically significant toxicities for one or both
of the bioassays when compared with the Carr Inlet reference
area (Figure 3.49).
• Ten of the sites were toxic in both bioassays. These sites
were located in Hylebos Waterway, City Waterway, St. Paul
Waterway, and on the Ruston-Pt. Defiance Shoreline.
• Overall, there was good agreement between the two bioassays,
especially as the toxic response exceeded 50 percent.
• Dilution bioassays indicated that in some areas (e.g., Stations
SP-14, RS-18/19, CI-11) the sediments were so toxic that
a 90 percent dilution was not sufficient to reduce toxicities
to reference levels.
• Oyster larvae abnormalities at some of these highly toxic
sites may have been due in part to low dissolved oxygen
resulting from high organic content of the sediments. The
amphipod mortalities at Station SP-14 may have also resulted
from low dissolved oxygen.
3.4 FISH ECOLOGY
3.4.1 Introduction
This section provides a description of general characteristics of
the total demersal fish assemblages and the English sole populations sampled
at 17 trawl transects in Commencement Bay and Carr Inlet (see Section 2.6).
The total assemblages in Commencement Bay and Carr Inlet are compared with
respect to species composition, species number, species diversity, and
total abundance. English sole populations in Commencement Bay and Carr
Inlet are compared with respect to median length, abundance, sex ratio,
and condition. Finally, results of the present study are compared with
historical data collected in Commencement Bay.
3.4.2 Total Fish Assemblages
3.4.2.1 Species Composition--
A total of 6,686 fishes, representing 17 families and 40 species,
was sampled in this study (Table 3.31). Commencement Bay study areas yielded
4,951 individuals and 38 species, whereas 1,735 fishes and 13 species were
3.140
-------
U)
• NO SIGNIFICANT RESPONSE
• AMPHIPOD OR OYSTER LARVAE
SIGNIFICANT RESPONSE
A AMPHIPOD AND OYSTER LARVAE
SIGNIFICANT RESPONSE
COMMENCEMENT
BAY
COMMCNCEMCNT
CITY
WATERWAY
Figure 3.49. Summary spatial patterns of significant
bioassay responses.
-------
TABLE 3.31. RELATIVE ABUNDANCES OF FISHES CAPTURED IN
COMMENCEMENT BAY AND CARR INLET
Family
Equal idae
Rajidae
Chimaeridae
Clupeidae
Engraulidae
Batrachoididae
Gadidae
Zoarcidae
Embiotocidae
Bathymasteridae
Stichaeidae
Scorpaenidae
Hexagrammidae
Cottidae
Agonidae
Bothidae
Pleuronectidae
Species
Squalus acanthias
Raja rhina
Hydro! agus colliei
Clupea harengus
pa 1 1 a?i
Engraulis mordax
mordax
Porichthys notatus
Gadus macrocephalus
Merluccius productus
Microgadus prox Irons
Lycodopsis pacifica
Cymatogaster aggregata
Embiotoca lateral is
Rhacochilus vacca
Ronquilus jordani
Lumpenus sagitta
Sebastes auriculatus
Sebastes caurinus
Sebastes maliger
Sebastes melanops
Hexagrammos stelleri
Ophiodon elongatus
Chitonotus pugetensis
Enophrys bison
Leptocottus armatus
Scorpaenichthys
marmoratus
Agon ops is emmelane
Agonus acipenserinus
Citharichthys sordidus
Citharichthys stigmaeus
Eopsetta jordani
Glyptocepjialus zachirus
HippogTossoides
elassodon
Inopsetta •ischyra
Lepidopsetta bil ineata
Lyopsetta exilis
Microstomus pacificus
Parophrys vetulus
Platichthys stellatus
Pleuronichthys coenosus
Psettichthys
melanostictus
Relative Abundance (X)
Common Name Commencement Carr
Bay Inlet
spiny dogfish
longnose skate
spotted ratfish
Pacific herring
northern anchovy
plainfin midshipman
Pacific cod
Pacific hake
Pacific tomcod
blackbelly eelpout
shiner perch
striped seaperch
pile perch
northern ronquil
snake prickleback
brown rockfish
copper rockfish
quillback rockfish
black rockfish
whitespotted
green! ing
lingcod
roughback sculpin
buffalo sculpin
Pacific staghorn
sculpin
cabezon
northern spearnose
poacher
sturgeon poacher
Pacific sanddab
speckled sanddab
petrale sole
rex sole
flathead sole
hybrid sole
rock sole
slender sole
Dover sole
English sole
Starry flounder
C-0 sole
sand sole
TOTAL CATCH
0.1
2.3
2.1
a
0.1
a
0.1
4.3
1.5
0.6
0.1
0.1
0.3
0.3
0.1
a
0.6
a
0.2
0.1
0.6
0.1
1.1
a
a
2.7
0.4
a
a
3.9
a
13.8
0.2
7.6
55.6
0.4
0.1
0.4
4,951
0.1
0.2
5.6
0.3
0.1
0.2
1.7
25.0
0.4
65.8
0.3
0.2
0.1
1,735
<0.1 percent.
3.142
-------
captured in Carr Inlet. Much of this discrepancy in catches resulted primarily
from the larger sampling effort expended in Commencement Bay (15 transects)
compared to Carr Inlet (2 transects), but may also have been partly due
to increased habitat complexity (e.g., pilings, rocks, debris) in Commencement
Bay.
The fish assemblages sampled in both Commencement Bay and Carr Inlet
were dominated by pleuronectids (82.0 and 91.8 percent, respectively).
The most abundant pleuronectids were English sole (55.6 and 65.8 percent,
respectively) and rock sole (13.8 and 25.0 percent, respectively).
3.4.2.2 Assemblage Characteristics--
Individual study areas within Commencement Bay were compared qualitatively
with the Carr Inlet reference area on the basis of three major characteristics
of fish assemblages: total abundance, total number of species, and species
diversity (Figure 3.50). The latter parameter was represented by the Shannon-
Wiener Index (H1; Shannon and Weaver 1949). For study areas including
more than one trawl transect (Hylebos, Blair, and City Waterways; Ruston-
Pt. Defiance Shoreline; and Carr Inlet), the mean value of all transects
within each area was considered for each assemblage characteristic.
For six of the eight Commencement Bay study areas, total abundance
of fish assemblages was over twice as large as that in Carr Inlet (60 fishes/
100 m). Only Hylebos Waterway and Ruston-Pt. Defiance Shoreline had abundances
similar to that in Carr Inlet. Total numbers of species in all Commencement
Bay study areas (range of 10.0 to 14.5) were relatively similar to that
in Carr Inlet (10.5). Diversity indices of fish assemblages in all Commence-
ment Bay study areas were greater than that in Carr Inlet (0.96). Diversity
indices in four of the eight study areas (Hylebos, Milwaukee, and City
Waterways, and the Ruston-Pt. Defiance Shoreline) exceeded that in Carr
Inlet by a factor of 1.5 or more.
In summary, fish assemblages in Commencement Bay study areas generally
were more abundant and more diverse than those in Carr Inlet. Total numbers
of species were similar among all areas. Although these comparisons are
largely descriptive, they show no indication that the gross characteristics
of fish assemblages in Commencement Bay were negatively affected by chemical
contamination. The relatively high abundances of demersal fishes in the
Commencement Bay waterways may be a result of high abundances of benthic
macroinvertebrates in the area. English sole have been shown to prefer
cirratulid polychaetes and molluscs as prey items (Becker 1984). Abundances
of both of these invertebrate groups are enhanced in Commencement Bay relative
to Carr Inlet, thus providing a rich food supply for bottom-feeding fishes.
3.4.3 English Sole Populations
3.4.3.1 Length Distribution--
As shown in Section 3.4.2.1 English sole was the most abundant species
in both Commencement Bay and Carr Inlet, accounting for 55.6 and 65.8 percent
(respectively) of overall assemblages. Although relative abundances of
English sole were similar between the two embayments, length distributions
of captured fish (Figure 3.51) were significantly different (P<0.001,
3.143
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300 -t
o
o
UJ
o
m
250 -
200-
150-
100-
50-
20 T
CO
LLJ
O
UJ
0.
CO
LL
O
O
"Z.
15 -
10-
5'
0
2.0 -i
CO
DC
UJ
5 a5
HY BL SI Ml ^ SP MD Cl RS
PI)
CR
STUDY AREA
Figure 3.50.
Comparisons of major characteristics of fish
assemblages from Commencement Bay study areas
with those of the assemblage from Carr Inlet.
3.144
-------
cn
to
c
ro
CO
in
o i—
Q) fD
-a 3
fD
Q. -»>
-S
_i. n>
3 -0
c
O fD
a 3
-s o
-s *<
>— i a.
3 -••
— • i/>
n> <-(•
n< cr
3 c
a. c-t-
o o
o 3
a> o
3 -h
n
n> m
3 3
fD UD
3 — '
rt- -••
l/>
CX3 3-
O>
i< l/>
• O
«^
fD
co
c
CO
m
o
i
I
8
g
m
CO
PERCENT
O
_L
8
I
m
z
Q
o
= 2O
« E O
i» i s
§ z m
11 z
In O
M m
i 5
1
PERCENT
m
-------
Mann-Whitney U-test). Median length in Carr Inlet (14.9 cm) was substantially
lower than that in Commencement Bay (25.2 cm) because populations in the
former embayment were dominated by young fish. For example, fish smaller
than 20 on accounted for over 80 percent of the population in Carr Inlet,
but only 4 percent of the population in Commencement Bay. Ihis size discrepancy
probably arises from the fact that juvenile English sole prefer shallow
sandy habitats as nursery areas (Ketchen 1956). Thus, the muddy nature
and altered benthos of most areas sampled in Commencement Bay may be suitable
for adult English sole, but largely unacceptable for younger individuals.
The large differences in median length of English sole between Commencement
Bay and Carr Inlet underline the value of setting a minimum size (i.e.,
an index of age) limit for histopathological analysis. For instance, if
fish had been selected randomly for this analysis, most individuals subsampled
from Carr Inlet would likely be smaller (and thus younger) than those taken
from Commencement Bay. Because several liver disorders in English sole
are functions of age (e.g., Mai ins et al. 1982; McCain et al. 1982; Section
3.5.5 of this study), comparisons of prevalences of these conditions between
embayments would be strongly biased by the different age distributions
of the subsampled fish.
3.4.3.2 Abundance--
At five of the eight Commencement Bay study areas (Blair, Sitcum,
St. Paul, Middle, and City Waterways), English sole abundance was more
than twice that in Carr Inlet (mean of 28.9 fish/100 m) (Figure 3.52).
The Ruston-Pt. Defiance Shoreline was the only study area in which English
sole abundance was lower than that in Carr Inlet. The trawl transect having
the greatest abundance of this species in both embayments (498.3 fish/100 m)
was BL70, at the mouth of Blair Waterway. The lowest abundance in the
study (2.3 fish/100 m) occurred at Transect RS72, off Pt. Defiance. These
data indicate that, except for the Ruston-Pt. Defiance Shoreline, the Commence-
ment Bay study areas generally attracted considerably more English sole
than did the reference area. A possible explanation for this pattern is
that most of the Commencement Bay study areas support considerably higher
standing crops of English sole prey (i.e., benthic invertebrates) than
does Carr Inlet (see Section 3.2).
3.4.3.3 Sex Ratio--
As noted previously (Section 2.6), sex was examined in all 1,020 English
sole subsampled for histopathological analysis. However, sex could not
be distinguished for 13 individuals (8, 3, 1, and 1 from Trawl Transects
CI72, CI71, MD70, and RS70, respectively). To determine whether sex ratios
varied with the physical characteristics of sediments at each study area,
the male percentages of English sole populations were compared with the
fine-grained (i.e., silt and clay) fraction of sediments at all study areas
using Spearman's rank correlation coefficient (rs).
Male percentages were significantly correlated (P<0.05) with percent
fine-grained sediments in a positive direction (Figure 3.53). Percentages
ranged from 20.8 at Carr Inlet (12.2 percent fine-grained sediments) to
98.3 in Sitcum Waterway (78.8 percent fine-grained sediments). This same
pattern was found by Becker (unpublished) for English sole (>150 mm TL)
3.146
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250—1
200 —
O
O 150
LU
O
1
CO
<
100-
50-
HY BL SI
Ml A SP MD Cl RS
PU
CR
STUDY AREA
Figure 3.52.
Comparison of abundances of English sole from
Commencement Bay study areas with the abun-
dance from Carr Inlet.
3.147
-------
at
HI
o
cc
uu
100 -
90 -
80 -
70-
60 -
50 -
40 '
30 -
20 -
10 -
10 20 30 40 50 60 70 80 90 100
PERCENT FINES
Figure 3.53.
Comparison of male percentages of English sole
populations with fine-grained sediment frac-
tions (silt plus clay) using the Spearman rank
correlation coefficient (rs).
3.148
-------
350-n
300-
250-
3 200-1
t-
150
100 —
50—<
CARR INLET (n = 25)
COMMENCEMENT BAY (n = 601)
MALES
350—1
300-
250 —I
200-^
150 -J
100 —
50 —
23 24 25 26 27 28 29 30 31 32 33 34
CARR INLET (n = 95)
COMMENCEMENT BAY (n = 286}
FEMALES
23 24 25 26 27 26 29 30 31 32 33 34
LENGTH (cm)
Figure 3.54. Comparisons of weight-length relationships of
male and female English sole captured in
Commencement Bay and Carr Inlet.
3.150
-------
ones common to both studies. Sizes of English sole from the present study
were based on all fish collected, whereas male percentages were based only
on those subsampled for histopathological analysis.
Size distributions at both stations did not differ significantly (P>0.05,
Mann-Whitney U-test) between the two studies (Figure 3.55). In both cases,
the difference in median length between studies was less than 1 cm. As
with median length, male percentages did not differ significantly (P>0.05,
2x2 contingency test) between studies at both stations. Male percentages
in 1981 and 1984 were 81.4 and 73.1 (respectively) in City Waterway, and
95.7 and 98.3 (respectively) in Sitcum Waterway.
The observed similarities of median sizes and male percentages between
1981 and 1984 suggest that, although most adult English sole migrate seasonally
(Ketchen 1956), the same population may utilize the Commencement Bay waterways
each year. If this supposition is correct, it would imply that these fish
could be exposed to waterway contaminants for a number of years, and thereby
be susceptible to the negative consequences that may result from long-term
contact with chemical contaminants.
3.4.4 Summary
• English sole dominated the demersal fish assemblage in both
Commencement Bay and Carr Inlet, accounting for 55.6 and
65.8 percent (respectively) of each assemblage.
• Demersal fish assemblages at the eight Commencement Bay
study areas generally were more abundant and more diverse
than the assemblage in Carr Inlet. By contrast, total number
of species was similar among all areas sampled.
• English sole sampled in Commencement Bay were significantly
larger (P<0.05) than conspecifics collected in Carr Inlet.
• Abundance of English sole at five of the eight Commencement
Bay study areas exceeded the abundance in Carr Inlet by
a factor of two or more. The Ruston-Pt. Defiance Shoreline
was the only study area having a lower abundance than Carr
Inlet.
t The male-to-female ratio of English sole populations correlated
significantly (P<0.05) with percent fine-grained sediment.
t Condition (i.e., weight-at-length) of all male and most
female English sole was greater in Commencement Bay than
in Carr Inlet.
t Length and sex ratio of English sole in City and Sitcum
Waterways did not differ significantly (P<0.05) between
the present study and historical data collected 3 yr earlier.
3.151
-------
30-1
UJ
O
cc
UJ
a.
20-
10-
CITY WATERWAY
1984 n = 197, MEDIAN
1981 n = 211, MEDIAN
(P>.05)
25.5cm
25.9cm
LU
O
a:
LU
a.
30 -|
20-
10 -
SITCUM WATERWAY
1984 n = 131, MEDIAN = 27.4cm
1981 n = 103, MEDIAN = 26.7cm
(P>.05)
12 16 20 24 28 32 36
TOTAL LENGTH (cm)
40
Figure 3.55.
Comparisons of length distributions of English
sole captured in City and Sitcum Waterways
during 1981 and 1984 using the Mann-Whitney
U-test.
3.152
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3.5 FISH HISTOPATHOLOGY
3.5.1 Introduction
This section presents the results of histopathological analyses conducted
on the livers of the 1,020 English sole subsampled at 17 trawl transects
in Commencement Bay and Carr Inlet (see Figure 2.6 in Section 2.1). Grossly
visible external abnormalities found on the subsampled fish are described
first. The kinds of liver lesions considered in this study are described
next. The relationships of these lesions to sex and age of the fish are
then determined so that, if necessary, these potential confounding factors
can be removed before lesion prevalences in Commencement Bay are compared
with those in Carr Inlet. Lesion prevalences based on Commencement Bay
as a whole, the eight study areas within the bay, and the individual trawl
transects within the larger study areas are then compared statistically
with prevalences in Carr Inlet. Finally, results of the present study
are compared with historical data collected in Commencement Bay.
3.5.2 External Abnormalities
Although this study focused on microscopic pathological conditions
of the liver, grossly visible external abnormalities of the 1,020 English
sole subsampled for histopathological analysis were also recorded. The
two most common external abnormalities in English sole found in Puget Sound
in the past and suspected of resulting from chemical contamination are
skin tumors (i.e., angioepithelial nodules, angioepithelial polyps, and
epidermal papillomas) and fin erosion. None of the 1,020 subsampled English
sole was affected by skin tumors, and only 9 individuals (0.9 percent)
showed confirmed cases of fin erosion. Thus, the fish subsampled in the
present study were relatively unaffected by these two kinds of external
abnormalities.
3.5.3 Classification of Liver Conditions
Over 50 types of gross and microscopic pathological conditions were
observed in the livers of the 1,020 English sole examined. These conditions
ranged from common parasitic infections to clearly identifiable neoplasms.
This study emphasized four lesion categories of unknown etiology (i.e.,
hepatic neoplasms, preneoplastic nodules, megalocytic hepatosis, and nuclear
pleomorphism). The causes of these disorders are unknown. It is possible
that they are induced by chemical contaminants in the environment. Moreover,
morphologically similar lesions have been induced in laboratory mammals
and fishes by exposure to toxic and/or carcinogenic chemicals (Maiins
et al. 1984). Each of the four lesion categories is described in the following
sections.
3.5.3.1 Hepatic Neoplasms--
Several kinds of neoplasm have been described in English sole. Each
one is discussed separately.
Liver Cell Adenoma—Liver cell adenomata are well-differentiated nodules
of normal architectural appearance that generally measure more than 1.0 mm
in diameter and that compress, but do not invade, the surrounding tissue.
3.153
-------
The margin of the adenoma is distinct from the normal surrounding tissue
and the tumor may be recognized by an absence of melanin macrophage centers
(MMCs) or other hepatic elements (e.g., pancreas). These hypercellular
foci contain hepatocytes with reduced or absent polarity, as well as reduced
or absent iron pigment. The cells are monomorphic with enlarged nuclei
and have variable staining patterns, ranging from basophilic to eosinophilic
or vacuolated. Sometimes multiple adenomata with different characteristics
may be seen within a single liver.
Hepatoeellular Carcinoma--Hepatocellular carcinomata are tumors charac-
terized by the presence of disorganized muralia and irregular borders.
They grow by expansion and by invasion into surrounding hepatic parenchyma.
The cells that constitute the tumor are pleomorphic, slightly hypertrophic
hepatocytes that lack cellular polarity. The cells are frequently anaplastic
and evidence an increased nuclearrcytoplasmic ratio. Their staining patterns
vary from primarily basophilic to occasionally eosinophilic or vacuolated.
The cells most often are arranged in a trabecular pattern, but occasionally
may assume a pseudotubular or solid pattern. The nodules are most often
devoid of MMCs or other hepatic tissue elements.
Cholangiocellular Carcinoma--Choiangiocellular carcinomata arise from
bile duct epithelium. They are invasive, often poorly differentiated neoplasms
with irregular borders. These tumors may occur alone or may be mixed with
hepatocellular carcinomata. In the more well-differentiated forms, the
tumors assume a relative degree of glandular organization with clearly
visible tubules or ducts. In less well-differentiated forms, there is
only a faint tendency to form ducts. The epithelia that constitute the
tumor are cuboidal to squamous, often spindle-shaped cells embedded in
a thin fibrous stroma. They are eosinophilic or amphophilic in well-differ-
entiated lesions, but basophilic in poorly differentiated tumors. The
nuclei are small (relative to those of hepatocytes), with reduced chromasia
and indistinct nucleoli.
3.5.3.2 Preneoplastic Nodules--
Three distinct cellular lesions appear in the livers of mammals exposed
to hepatocarcinogens: clear, eosinophilic, and basophilic nodules (Squire
and Levitt 1975; Stewart et al. 1980). These lesions are recognized by
their staining characteristics and by functional anomalies that can be
detected histochemically. These lesion types may occur singly, in pairs,
or all three simultaneously in a single liver. They may also be found
in tissue that contains neoplasms. These foci typically measure 1.0 mm
or less in diameter and are considered to represent preneoplastic steps
in the development of hepatocellular carcinomas.
Clear Cell Focus--Clear cell foci are discrete, spherical nodules
characterized by the apparent emptiness of their cellular cytoplasm. The
cytoplasm of the constituent cells is filled with vacuoles that appear
clear ("empty") when stained by conventional techniques (e.g., hematoxylin
and eosin). The foci are distinct from the surrounding parenchymal cells
even if they have a high degree of vacuolization. Histochemically, the
cells may contain glycogen or lipid. The lesions do not compress the adjacent
tissue.
3.154
-------
Eosinophilic Nodule--Foci of hepatocytes characterized by intense
eosinophilia are referred to as eosinophilic nodules (eosinophil ic hyper-
trophy). These foci are spherical, non-compressing structures that blend
imperceptibly into the surrounding muralia. In some systems, they elicit
a pronounced inflammatory/immunological response. The foci contain hyper-
trophic hepatocytes having eosinophilic cytoplasm, but that otherwise have
normal cellular characteristics. These foci typically do not contain MMCs.
In trout, the intense eosinophilia has been shown to result from an abundance
of smooth endoplasmic reticulum (Hendricks et al. 1984).
Basophilic Npdu1e--Basophilic nodules (hyperbasophilie foci) are discrete,
spherical foci (0.1-1.0 mm in diameter) that contain small, basophilic
hepatocytes. In trout, the basophilia has been shown to result from extensive
quantities of granular endoplasmic reticulum and free ribosomes. The foci
are non-compressing and grade imperceptibly into the adjacent parenchyma.
They typically contain no MMCs and may have reduced hemosiderin levels
in siderotic livers. These foci are believed to be a signal that neoplastic
transformation is complete (Hendricks et al. 1984).
3.5.3.3 Megalocytic Hepatosis--
Megalocytic hepatosis is a degenerative lesion of the hepatocellular
parenchyma that is characterized by a marked increase (two- to threefold)
in the nuclear and cellular diameters of affected hepatocytes in the absence
of cellular inflammatory responses (Malins et al. 1982). The nuclei of
affected cells are vesicular and hyperchromatic, and the cytoplasm is generally
eosinophilic and often shows associated changes such as hydropic degeneration
or hyalinization. Megalocytic hepatosis is often found in association
with altered MMCs, hemosiderois, or foci of hepatocellular regeneration.
This change is considered to be a degenerative condition that results from
toxic injury. It is not a proliferative lesion, nor is it considered to
be a preneoplastic focus.
3.5.3.4 Nuclear Pleomorphism--
Nuclear pleomorphism is a condition occasionally seen in hepatic tissue
undergoing degenerative changes. The condition, which occurs in hepatocytes,
is characterized by increased nuclear diameter with no attendant increase
in cellular diameter. Nuclei are not considered to be pleomorphic unless
there is at least a threefold variation in nuclear diameter from the smallest
to the largest nucleus in the tissue. This condition is considered to
be degenerative and non-proliferative.
3.5.4 Effects of Sex
To determine whether any of the four kinds of liver lesions described
previously occurred more frequently in male or in female English sole,
the sex distribution of fish having each condition was compared with the
sex distribution of all English sole examined from Commencement Bay (Table 3.32)
using a 2x2 contingency formulation and the chi-square criterion. Sex
distributions for all four lesion types were not significantly different
(P>0.05) from the overall distribution in Commencement Bay (Table 3.32),
indicating that both sexes were similarly affected by these disorders.
3.155
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TABLE 3.32. COMPARISONS OF SEX DISTRIBUTIONS OF COMMENCEMENT
BAY ENGLISH SOLE HAVING VARIOUS KINDS OF LIVER LESION WITH THE
SEX DISTRIBUTION OF ALL ENGLISH SOLE SAMPLED IN COMMENCEMENT BAYa'°
Number (Percent) Having Each Condition
Liver Lesion Males Females Significance0
Hepatic neoplasms
Preneoplastic nodules
Megalocytic hepatosis
Nuclear pleomorphisms
20
76
60
25
(3.3)
(12.6)
(10.0)
(4.2)
5
38
37
17
(1.7)
(13.0)
(12.9)
(5.9)
ns
ns
ns
ns
a Overall Commencement Bay distribution was 601 males and 286 females.
b Comparisons were made using a 2x2 contingency formulation and the chi-square
criterion. (Comparisonwise significance level = 0.0125).
c ns = P>0.05. (experimentwise).
3.156
-------
3.5.5 Effects of Age
As noted in Section 2.6, Malins et al. (1982) and McCain et al. (1982)
found that prevalences of liver lesion in English sole were substantially
lower in younger than in older fish. Because of this age dependence, only
larger (and thus older) English sole were subsampled for histopathological
analysis in the present study (see Section 2.6). Using a 225-mm minimum
size criterion, only 6 of the 950 (0.6 percent) English sole aged in this
study were less than 3 yr old. Seventy (6.9 percent) fish could not be
aged because their otoliths were either lost in the field or were unreadable.
To determine whether prevalence of each of the four lesions considered
in the present study showed a monotonic increase with age in the aged English
sole (>2 yr old) subsampled from Commencement Bay (n=837), prevalence of
each disorder was compared with fish age using Spearman's rank correlation
coefficient (rs). Because none of these disorders showed a sex-related
bias (see Section 3.5.4), fish were not stratified by sex in this analysis.
Prevalences of hepatic neoplasms and preneoplastic nodules were signifi-
cantly correlated (P<0.05) with fish age (Figure 3.56). Neoplasm prevalence
ranged from 0 (age 3) to 5.0 (age >7) percent and, aside from a slight
decline between ages 4 and 5, increased monotonically with fish age. Preva-
lences of preneoplastic nodules increased monotonical ly with age, ranging
from 5.7 (age 3) to 17.5 (age >7) percent.
Prevalences of megalocytic hepatosis and nuclear pleomorphism did
not correlate significantly (P>0.05) with fish age (Figure 3.56). Although
prevalence of megalocytic hepatosis steadily increased from 9.1 to 13.5
percent between ages 3 and 5, it declined slightly to 12.6 percent at age
6 and then decreased dramatically to 5.6 percent at ages >7. By contrast,
prevalence of nuclear pleomorphism was quite stable across age groups,
ranging from 3.9 to 5.6 percent.
3.5.6 Spatial Patterns of Individual Disorders^
The primary goal of the histopathological analysis was to determine
whether English sole from Commencement Bay exhibited significantly different
(P<0.05) prevalences of liver lesions than conspecifics from Carr Inlet
(i.e., the reference site). Comparisons were made using a 2x2 contingency
formulation and the chi-square criterion. Spatial patterns were considered
on three scales: by embayment, by study area, and by trawl transect within
each larger study area (Hylebos, Blair, and City Waterways, and the Ruston-
Pt. Defiance Shoreline). Because the four lesions considered in this study
did not show a sex bias (see Section 3.5.4), no corrections were made for
differences in sex distributions between the reference site and Commencement
Bay. By contrast, because three of the lesions were positively correlated
with age (see Section 3.5.5), age distributions of English sole from Commence-
ment Bay were compared with that in Carr Inlet before histopathological
comparisons were made.
3.157
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To test for age differences between English sole in Commencement Bay
and Carr Inlet, age distributions were compared between embayments using
the Mann-Whitney U-test. Separate comparisons were made for each scale
of analysis (i.e., by embayment, study area, and transect). Age distributions
of English sole from all of Commencement Bay, from two study areas (Blair
and Sitcum Waterways), and from three trawl transects within the larger
study areas (BL70, BL71, and BL72) differed significantly (P<0.05) from
the age distribution in Carr Inlet. In each case, median age was greater
in Commencement Bay. To correct for these age differences, the largest
fish from each Commencement Bay site were eliminated sequentially until
the median age of the remaining distribution did not differ significantly
(P>0.05) from that in Carr Inlet. Using this approach, 47 fish were eliminated
from the total Commencement Bay sample, 46 and 1 fish were removed from
the distributions in Blair and Sitcum Waterways (respectively), and 17,
9, and 3 fish were removed from the individual samples at Transects BL70,
BL71, and BL72, respectively.
3.5.6.1 Patterns Based on Embayments--
Prevalences of the four lesion categories in age-corrected samples
of English sole from Commencement Bay and Carr Inlet are presented in Figure
3.57. Occurrences of hepatic neoplasms and nuclear pleomorphism were restricted
to Commencement Bay fish. The most frequently observed lesion categories
in English sole from both areas were preneoplastic nodules and megalocytic
hepatosis. Prevalences of three of the four liver conditions (preneoplastic
nodules, megalocytic hepatosis, and nuclear pleomorphism) were significantly
higher (P<0.05) in Commencement Bay than in Carr Inlet. On a bay-wide
basis, the prevalence of hepatic neoplasms was not statistically elevated
in Commencement Bay fish when compared to Carr Inlet. On a bay-wide basis,
the prevalence of hepatic neoplasms was not statisticaly elevated in Commence-
ment Bay fish when compared to Carr Inlet.
3.5.6.2 Patterns Based on Study Areas--
Prevalence of hepatic neoplasms was not significantly different (P>0.05)
from that in Carr Inlet (0 percent) at any of the eight Commencement Bay
study areas (Table 3.33). The highest incidence of hepatic neoplasms in
Commencement Bay study areas (8.3 percent) was in Middle Waterway, whereas
the lowest value (0 percent) was found along Ruston-Pt. Defiance Shoreline.
Prevalence of preneoplastic nodules was significantly different (P<0.05)
fron that in Carr Inlet (5.8 percent) only in Middle Waterway (26.7 percent).
The lowest incidence of preneoplastic nodules in Commencement Bay study
areas (6.6 percent) was found in Blair Waterway.
Prevalence of megalocytic hepatosis was significantly different (PO.05)
from that in Carr Inlet (0.8 percent) at four Commencement Bay study areas:
Hylebos (18.3 percent), Milwaukee (16.7 percent), Middle (15.0 percent),
and Blair (11.9 percent) Waterways. The lowest incidence of this disorder
in Commencement Bay study areas (5.0 percent) was found in St. Paul Waterway.
As with preneoplastic nodules, prevalence of nuclear pleomorphism
was significantly different (P<0.05) from that in Carr Inlet (0 percent)
only in Middle Waterway (10.0 percent). Prevalences of this disorder in
3.159
-------
LU
o
z
ai
ai
15
14
13
12
11
9
8
7
6
5
4
3
2-
1 •
0
COMMENCEMENT BAY n = 853)
CARR INLET (n = 120)
# P < 0.05
ns P > 0.05
ns
(0)
]
(0)
fif-
LIVER LESION
Figure 3.57.
Comparisons of prevalences of six liver disor-
ders between English sole from Commencement
Bay and Carr Inlet using a 2 X 2 contingency
test. (Critical chi-square = 3.84.)
3.160
-------
TABLE 3.33. COMPARISONS OF PREVALENCES OF FOUR LIVER LESIONS BETWEEN
ENGLISH SOLE FROM STUDY AREAS IN COMMENCEMENT BAY AND CARR INLET
CM
Study
Area
Hylebos
Waterway
Blair
Waterway
Sitcum
Waterway
Milwaukee
Waterway
St. Paul
Waterway
Middle
Waterway
City
Waterway
Ruston-
Pt. Defiance
Shoreline
Carr Inletc
Sample
Size9
180
134
(180)
59
(60)
60
60
60
120
180
120
Hepatic
Neoplasms
2.8
0.8
(3.3)
5.1
(5.0)
3.3
1.7
8.3
0.8
0
0
Percent of Fish
Preneoplastic
Nodules
13.3
7.5
(9.4)
18.6
(18.3)
15.0
16.7
26.7*
8.3
10.6
5.8
Having Each Condition*5
Megalocytic
Hepatosis
18.3*
12.7*
(11.1)
10.2
(10.0)
16.7*
5.0
15.0*
6.7
5.6
0.8
Nuclear
Pleomorphism
5.6
4.5
(6.1)
5.1
0
5.0
10.0*
3.3
2.8
0
a Sample sizes in Blair and Sitcum Waterways were reduced when age distributions
were adjusted (see text for explanation). Unadjusted values are given
in parentheses.
b An asterisk denotes that a prevalence was significantly different (P<0.05)
from that at Carr Inlet. (Comparisonwise significance level = 0.0031).
c Reference area.
-------
the remaining Commencement Bay study areas were less than 6 percent, with
the lowest value (0 percent) found in Milwaukee Waterway.
English sole from Middle Waterway had the greatest number (3) of signif-
icantly elevated (P<0.05) liver lesions in Commencement Bay. These included
preneoplastic nodules, megalocytic hepatosis, and nuclear pleomorphism.
Fish from Hylebos, Blair, and Milwaukee Waterways had significantly elevated
levels of only megalocytic hepatosis. Finally, fish from St. Paul and
City Waterways and Ruston-Pt. Defiance Shoreline did not have significantly
elevated levels of any of the four lesions considered.
3.5.6.3 Patterns Based on Trawl Transects--
Prevalences of hepatic neoplasms, preneoplastic nodules, and nuclear
pleomorphism were not significantly different (P>0.05) from those in Carr
Inlet at any of the 11 trawl transects in Commencement Bay (Table 3.34).
Transects having the highest prevalence of each disorder were HY71 (neoplasms
- 6.7 percent), RS70 (preneoplastic nodules - 18.3 percent), and HY70 (nuclear
pleomorphism - 8.3 percent).
Prevalence of megalocytic hepatosis was significantly different (P<0.05)
from that in Carr Inlet at all three transects in Hylebos Waterway (HY70,
71, and 72), at two of the three transects in Blair Waterway (BL70 and
71), and at one of the three transects along Ruston-Pt. Defiance Shoreline
(RS70). The highest incidence of this disorder at a trawl transect within
a Commencement Bay study area (26.7 percent) was at HY70, and the lowest
value (0 percent) was at RS71.
When lesion prevalence in areas with multiple trawl samples is examined
on a trawl sample basis rather than on an overall area basis, the only
differences occurred in Blair Waterway and along the Ruston-Pt. Defiance
Shoreline. In these two areas, there is evidence of spatial gradients
in the prevalences of megalocytic hepatosis. Although Blair Waterway had
an overall significant elevation in megalocytic hepatosis, the prevalence
of this lesion was low and not significantly different from Carr Inlet
(P>0.05) near the waterway mouth. Along the Ruston-Pt. Defiance Shoreline
the overall prevalence of megalocytic hepotosis was not significantly elevated.
However, the individual trawl site nearest the mouth of City Waterway displayed
a statistically significant elevation (P<0.05) in the lesion prevalence.
3.5.7 Spatial Patterns of Fish Having One or More Major Lesion
To construct a single index representing the prevalence of possible
contaminant-induced liver lesions in English sole from Commencement Bay
and Carr Inlet, the number of fish having one or more of the four liver
lesions was calculated. Because many fish were afflicted with more than
one type of lesion, the number of fish having one or more of the four lesions
is less than would be calculated by simply summing the prevalences of the
individual lesion types. This index thus represents the actual number
of afflicted fish, rather than the number of afflictions. Comparisons
between prevalences of fish having one or more major lesions in Commencement
Bay and Carr Inlet were made using a 2x2 contingency formulation and the
chi-square criterion.
3.162
-------
TABLE 3.34. COMPARISONS OF PREVALENCES OF FOUR LIVER LESIONS BETWEEN
ENGLISH SOLE FROM TRAWL TRANSECTS IN COMMENCEMENT BAY AND CARR INLET
u>
a\
u>
Trawl
Transect
HY70
HY71
HY72
BL70
•
BL71
BL72
CI70
CI72
RS70
RS71
RS72
CR70 and 7K
Sample
Sizea
60
60
60
43
(60)
51
(60)
57
(60)
60
60
60
60
60
120
Heptatic
Neoplasms
0
6.7
1.7
2.3
(8.3)
0
(0)
0
(1.7)
1.7
0
0
0
0
0
Percent of Fish Having
Preneoplastic
Nodules
13.3
15.0
11.7
11.6
(16.7)
5.9
(8.3)
3.5
(3.3)
6.7
10.0
18.3
8.3
5.0
5.8
Each Condition'1
Megalocytic
Hepatosis
26.7*
15.0*
13.3*
14.0*
(13.3)
19.6*
(16.7)
3.5
(3.3)
10.0
3.3
11.7*
0
5.0
0.8
Nuclear
Pleomorphism
8.3
0.5
3.3
7.0
(10.0)
5.9
(5.0)
1.8
(3.3)
5.0
1.7
5.0
0
3.3
0
a Sample sizes in Blair Waterway were reduced when age distributions were
adjusted (see text for explanation). Unadjusted values are given in paren-
theses.
b An asterisk denotes that a prevalence was significantly different (P<0.05)
from that at Carr Inlet. (Comparisonwise significance level = 0.0023).
c Reference area.
-------
Prevalence of fish having one or more lesions was significantly different
(PO.05) from that in Carr Inlet (6.7 percent) at five of the eight Commencement
Bay study areas (Figure 3.58): Hylebos, Blair, Sitcum, Milwaukee, and
Middle Waterways. Prevalence in Commencement Bay study areas was highest
(40.0 percent) in Middle Waterway and lowest (13.3 percent) in City Waterway.
Within the larger Commencement Bay study areas (i.e. Hylebos, Blair,
and City Waterways, and the Ruston-Pt. Defiance Shoreline), prevalence
of fish having one or more lesions (Figure 3.58) was significantly different
(P<0.05) from that in Carr Inlet at all three trawl transects in Hylebos
Waterway (HY70, 71, and 72), at two transects in Blair Waterway (BL70 and
71), and at one transect along Ruston-Pt. Defiance Shoreline (RS70). Prevalence
at Commencement Bay transects was highest (33.3 percent) at HY70 and lowest
(7.0 percent) at BL72.
In general, prevalences of fish having one or more lesions at trawl
transects showed patterns similar to those of their respective larger study
area. However, there were two exceptions. First, prevalence at BL72 (7.0
percent) was almost as low as that in Carr Inlet, whereas prevalence in
the entire Blair Waterway (20.9 percent) was significantly different (PO.05)
from that at the reference area. By contrast, prevalence at RS70 (26.7
percent) was significantly different (P<0.05) from that at Carr Inlet,
whereas overall prevalence along Ruston-Pt. Defiance Shoreline (15.6 percent)
was not significantly different (P>0.05) from that at the reference area.
3.5.8 Fish Condition Comparisons
To examine whether Commencement Bay English sole with hepatic lesions
exhibited reduced condition (see Section 3.4.3.4) relative to conspecifics
without these lesions, weight-at-length (WAL) values of these two groups
(stratified by sex) were compared using regression analysis. Weight and
length values for all fish were log-transformed and least-squares linear
regression lines were calculated (cf. Ricker 1975). Regression lines for
fish with and without lesions were tested for coincidence using the Z test
(Kleinbaum and Kupper 1978).
For both sexes, the slopes and y-intercepts of the regression equations
for fish with and without hepatic lesions did not differ significantly
(P>0.05, Table 3.35). Each pair of regression lines can therefore be considered
coincident. Thus, English sole with hepatic lesions did not exhibit reduced
condition relative to conspecifics without lesions.
3.5.9 Comparisons with Historical Data
Most historical studies of liver disorders in English sole from Puget
Sound have been conducted by Dr. Donald C. Mai ins and his associates at
the Environmental Conservation Division of the Northwest and Alaska Fisheries
Center of NMFS. As mentioned previously (Section 2.6), all abnormal liver
conditions observed in the present study were independently verified by
the chief pathologist of Mai ins1 group. Although this intercalibration
procedure ensured that consistent classifications of liver disorders were
made, direct comparisons of results of the present study with data collected
in the past by Mai ins et al. (1980, 1982, 1984) are limited by several
additional factors. First, and perhaps foremost, is the fact that Malins
3.164
-------
-•• (D
3 3
<< 3
n>
to Cu
C
-J
n>
CO
00
c 3
-J "o
o, ->.
C-i. t/l
o o
-5 3
l/l
n> o
T3 -*i
Cu
Oi
3
O.
O
D»
T
-j. -j
O (D
<
— ' Oi
o> — •
l» O)
-"• 3
OO
3 ro
to to
)
-•• O
' 3 -h
• n o
3 3
to n>
— >
. _j. o
to -J
Q) I/) O
O -J
ro — i n>
n>
x o
.-*!-»»
1
PREVALENCE (%)
u
01
§
33
m
05
TJ
O
33
«.!..
.* *
33 _^:
**
TJ T3
A A
O O
o b
01 01
3 3
rn
H >
>
2
C/)
a
-------
TABLE 3.35. COMPARISONS OF WEIGHT-LENGTH REGRESSION COEFFICIENTS^
BETWEEN ENGLISH SOLE WITH LESIONS AND CONSPECIFICS WITHOUT LESIONS
Sex
Male
Female
Lesionb
absent
present
absent
present
Number
Sloped
of fishc b(S.
471
130
217
69
2.
2.
2.
2.
68
65
66
74
E.)
(0.
(0.
(0.
(0.
Y-Intercepte
Significance a(S.E.)
045)
ns
088)
066)
ns
101)
-4.
-4.
-4.
-4.
32
24
22
44
(0
(0
(0
(0
Significance
.109)
.214)
.162)
.248)
ns
ns
a Regression equations were based on log-transformed weights and lengths,
and comparisons were stratified by sex.
b Presence or absence of one or more of the following hepatic lesions:
neoplasms, preneoplastic nodules, megalocytic hepatosis, and nuclear pleo-
rnorphisms.
c Only fish from Commencement Bay were considered.
d The slopes (b) for each sex were compared using the Z test. The standard
error (S.E.) of each slope is given in parentheses, ns = P>0.05.
e The y-intercepts (a) for each sex were compared using the Z test. The
standard error (S.E.) of each intercept is given in parentheses, ns =
P>0.05.
3.166
-------
et al. (1980, 1982, 1984) included all age groups of English sole (including
fish less than Syr old) when calculating prevalences, whereas, by design,
almost all of the 950 fish aged in the present study (99.4 percent) were
at least 3 yr old. As shown by Mai ins et al. (1982), McCain et al. (1982),
and the present study (see Section 3.5.5), several liver conditions are
positively related to fish age. Thus, prevalences reported in the present
study are likely to be substantially higher than those found by Mai ins
et al. because of the exclusion of the youngest fish (i.e., <3 years old)
from the present study.
A second major limitation to intercpmparisons with historical data
arises from differences in sampling locations. As shown in the present
study, prevalences of liver disorders can vary dramatically over relatively
short distances. For example, the incidence of megalocytic hepatosis declined
by 11.7 percent between Transects HY70 and HY71 in Hylebos Waterway and
by 16.1 percent between Transects BL71 and BL72 in Blair Waterway (Table 3.32).
A third type of limitation to intercomparisons with historical data
is based on temporal differences. It is likely that seasonal or interannual
differences among studies would influence observed prevalences to some
degree. For instance, Malins et al. (1980) found that prevalence of megalocytic
hepatosis in English sole at Commencement Bay stations declined from winter
to summer, and then increased in fall. In addition, McCain et al. (1982)
found a significant decrease in the prevalence of hepatic neoplasms in
English sole from Sitcum Waterway between 1979 and 1983.
Given the above limitations, results of the present study and those
found by Malins et al. (1984) were only compared qualitatively. Prevalences
of the four lesions considered earlier (i.e., hepatic neoplasms, preneoplastic
nodules, megalocytic hepatosis, and nuclear pleomorphism) were compared
between the present study and that of Malins et al. (1984) at the three
areas of Commencement Bay common to both studies (Figure 3.59). Although
Malins et al. (1980) did not sample fish in Carr Inlet, two of their reference
stations were located in an adjacent embayment, Case Inlet. Because these
two embayments are morphologically similar, prevalences of liver disorders
were compared between them. Because Malins et al. (1980) pooled the prevalences
of nuclear pleomorphism with those of megalocytic hepatosis (Myers, M.,
9 January 1985, personal communication), data from the present study were
modified in a similar manner. Results from Malins et al. (1984) were taken
from Table III, and represent data pooled across four sampling periods
(winter, spring, summer, and fall) from 1979 to 1982.
As expected, prevalences of all three liver lesions generally were
higher in the present study than were those found by Malins et al. (1984;
Figure 3.59). However, the relative magnitudes of each condition across
different areas was quite similar between studies. In general, prevalence
of each disorder was at or close to 0 percent in Carr and Case Inlets.
The one exception was preneoplastic nodules in Carr Inlet, where a prevalence
of approximately 6 percent was found in the present study. For both studies,
prevalences of all three lesions reached their highest respective levels
in either Hylebos Waterway or the remaining Commencement Bay waterways.
Finally, prevalences along the Ruston-Pt. Defiance Shoreline of all three
lesions in both studies were intermediate in magnitude between prevalences
in the reference areas and those in the waterways.
3.167
-------
PRESENT STUDY
MALINS ET AL. (1984)
25
20'
15
ID-
S'
0
HEPATIC NEOPLASMS
(0) (0)
25
-------
The observed similarities between the spatial distributions of the
the three hepatic lesions found in the present study and those found by
Mai ins et al. (1984) 2-5 yr earlier imply that these patterns are real
(not spurious) and that they are quite stable temporally. This suggests
that the causes of the lesions may be localized within the overall study
area.
Because most adult English sole migrate to deeper water in winter
(Ketchen 1956; Miller et al. 1977), it is somewhat surprising that this
movement does not obscure the observed spatial patterns of lesion prevalence.
There exist several possible explanations for the persistence of these
patterns. First, fish having lesions may not migrate. If the lesions
indicate that a fish is in poor health, it is possible that affected individuals
do not have the stamina to undertake migration. However, this explanation
does not seem plausible because of the apparently normal condition factors
of English sole with hepatic lesions. A second possibility is that the
same individuals return to the same locality every year following over-
wintering. Although English sole have exhibited some degree of homing
ability (Day 1976), the precision with which these fish can relocate a
localized area is unknown. A third possibility is that lesions are rapidly
induced in a single season. Thus, an individual would only have to enter
a lesion-causing area during a single migration cycle, rather than returning
year after year, or permanently residing in the area. The strong age dependence
of hepatic neoplasms and preneoplastic nodules suggests that exposure to
lesion inducers must occur over several years. However, it could be that
older fish are less resistant to lesion induction (e.g., as part of senescence)
and therefore exhibit higher lesion prevalences than younger individuals
after a single exposure period. Although the lesion induction process
in English sole cannot be explained at present, it seems clear from this
study and Mai ins et al. (1984) that this process is highly dependent upon
spatial locations.
3.5.10 Summary
• Four kinds of hepatic lesions were considered in this study:
hepatic neoplasms, preneoplastic nodules, megalocytic hepatosis,
and nuclear pleomorphism.
• For all data pooled within Commencement Bay, prevalences
of preneoplastic nodules, megalocytic hepatosis, and nuclear
pleomorphism were significantly elevated (P<0.05) compared
to prevalences in Carr Inlet.
t Based on the eight Commencement Bay study areas, prevalences
of preneoplastic nodules and nuclear pleomorphism were
significantly elevated (P<0.05) only in Middle Waterway,
and prevalence of megalocytic hepatosis was significantly
elevated (P<0.05) in Hylebos, Blair, Milwaukee, and Middle
Waterways.
• Based on individual trawl transects within the larger study
areas (i.e., Hylebos, Blair, and City Waterways, and the
Ruston-Pt. Defiance Shoreline), prevalence of megalocytic
3.169
-------
hepatosis was significantly elevated (P<0.05) at all transects
in Hylebos Waterway (HY70, 71, and 72), at two transects
in Blair Waterway (BL 70 and 71), and at Transect RS70 along
the Ruston-Pt. Defiance Shoreline.
• Prevalences of hepatic neoplasms were not significantly
elevated (P<0.05) for all data pooled within Commencement
Bay, the eight study areas, or the individual trawl transects
when compared with prevalences in Carr Inlet.
t Prevalence of fish having one or more of the four hepatic
lesions was significantly elevated in Hylebos, Blair, Sitcum,
Milwaukee, and Middle Waterways (based on study areas) and
at HY71, HY72, BL71, BL72, and RS70 (based on trawl transects
within the larger study areas). Spatial patterns based
on fish having significantly elevated (P<0.05) prevalences
of one or more of the four lesions are summarized in Figure
3.60.
• Results of the present study were compared with historical
data collected by Malins et al. (1984). Absolute values
of the prevalences of hepatic neoplasms, preneoplastic nodules,
and megalocytic hepatosis in the present study were generally
larger than those found by Malins et al. (1984). However,
this discrepancy may be largely the result of different
age distributions of English sole sampled by the two studies.
By contrast with absolute values, the relative magnitudes
of lesions prevalences across areas were very similar between
the two studies. In both studies, prevalences were lowest
at reference sites, highest in the Commencement Bay waterways,
and intermediate in magnitude along the Ruston-Pt. Defiance
Shoreline.
3.6 BIOACCUMULATION
3.6.1 In trod u c t i on
Bioaccumulation studies were conducted as part of this investigation
to determine if sediment or water contaminants are accumulated in the tissues
of indigenous organisms. The specific objectives of these studies were
to:
• Determine if measurable concentrations of priority pollutants
and other substances (as were measured in sediment samples)
are present in organism tissues
• Determine if there are statistically significant elevations
in measured tissue contaminants in the Commencement Bay
study area when compared with the Carr Inlet reference area
• Collect data for use in an endangerment assessment to assess
risks to public health from ingestion of contaminated seafood
3.170
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Ql (p < 05> SIGNIFICANT LESION PREVELANCE
O (p > -05) NO SIGNIFICANT LESION PREVELANCE
COMMENCEMENT
BAY
co
•
t—•
•vl
METERS
1000
CITY
WATERWAY
Figure 3.60. Summary of areas having significantly elevated
prevalences of one or more hepatic lesions in
English sole.
-------
a Collect data for use in the decision-making approach to
identify and prioritize problem areas within Commencement
Bay.
Bioaccumulation studies were conducted on two species: English sole
(Parophrys vetulus) and cancrid crabs (Cancer spp). English sole were
selected for study because they live in direct contact with the sediments,
are relatively sedentary (compared to pelagic fish species), are abundant
in the waterways, and have been shown in previous studies (e.g., Gahler
et al. 1982) to accumulate sediment contaminants. Cancrid crabs also live
in direct contact with the sediments and provide an assessment of possible
differences between bioaccumulation in fishes and Crustacea.
3.6.2 Metals in Fish Muscle
Results of analyses of inorganic substances in English sole muscle
tissue are presented in Table 3.36. In general, the concentrations were
relatively homogeneous among study areas, and there were few cases in which
Commencement Bay fish displayed elevated concentrations relative to Carr
Inlet reference values. Statistical analyses using the Kruskal-Wal lis
test indicated no significant (P>0.05) overall differences in tissue concen-
trations among study areas for the following inorganic substances: antimony,
cadmium, chromium, nickel, and zinc. Several inorganic substances (i.e.,
arsenic, lead, and silver) actually displayed significantly (P<0.05) lower
concentrations in some Commencement Bay fish when compared with reference
concentrations.
The only two metals with significantly elevated tissue concentrations
in any Commencement Bay area relative to Carr Inlet were mercury and copper
(Table 3.36). Although mercury displayed relatively little overall variability
among areas (i.e., average concentrations of 42-87 ug/kg wet weight), its
within-area variability was also low. English sole from Hylebos Waterway
had significantly higher mercury levels than conspecifics from Carr Inlet,
even though the tissue mercury levels were only elevated by about 1.5 times
(81 vs. 55 ug/kg wet weight). No other study areas had significantly elevated
mercury levels when compared with reference values. Copper concentrations
were significantly elevated in fish from Sitcum and St. Paul Waterways
and the Ruston-Pt. Defiance Shoreline. Highest average copper concentrations
(346 ug/kg wet weight) occurred in fish from St. Paul Waterway.
Because of its widespread presence in Commencement Bay sediments,
arsenic was of special concern relative to potential bioaccumulation in
resident fishes. The results of this study indicate that arsenic is not
being accumulated by English sole in Commencement Bay at levels higher
than would be expected in uncontaminated areas of Puget Sound. Most of
the English sole collected in this study had muscle arsenic levels of 1-10
mg/kg wet weight, with occasional higher concentrations of 15-32 mg/kg
wet weight. The highest average arsenic concentration (7.9 mg/kg wet weight)
was measured in English sole from Carr Inlet. This high value resulted
in part from the fact that the overall maximum arsenic concentration of
32 mg/kg wet weight was also detected in the Carr Inlet samples. Statistical
analyses indicated that English sole from Hylebos, City, Milwaukee, and
Sitcum Waterways had significantly (P<0.05) lower muscle arsenic concentrations
than English sole from Carr Inlet.
3.172
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u>
TABLE 3.36. MEAN CONCENTRATIONS (mg/kg WET WEIGHT) OF INORGANIC
SUBSTANCES IN ENGLISH SOLE MUSCLE TISSUE
Arsenic
Carr Inlet 7.9
Hylebos Waterway <3.o
Blair Waterway 5.7
Site urn Waterway
-------
3.6.3 Metals In Crab Muscle
Crabs were relatively rare in the Commencement Bay Waterways and too
few were collected to obtain replicate samples at all sites. Dungeness
crabs were rare and could not be collected consistently for tissue analysis.
Therefore, rock crabs (Cancer spp.) were collected for tissue analyses
in many areas. Because of these limitations, statistical analysis of the
crab bioaccumulation data is not appropriate. Inspection of the mean values
for the crab data indicates, however, that the concentrations of most inorganic
substances were relatively homogeneous among sampling sites (Table 3.37).
Arsenic concentrations were less variable in the tissues of crabs
than in those from English sole, with individual muscle tissue concentrations
ranging from 0.75 to 3.5 mg/kg wet weight. Mean arsenic concentrations
from the waterways (1.2-2.9 mg/kg wet weight) displayed no apparent elevations
relative to the Carr Inlet samples (average of 2.4 mg/kg wet weight).
Crab muscle concentrations of chromium, copper, nickel, silver, and zinc
displayed similar patterns. For these metals, mean concentrations in crabs
from Commencement Bay were not more than about two times the Carr Inlet
reference concentration. A single crab from St. Paul Waterway had a cadmium
concentration of 0.620 mg/kg wet weight, about four times the average Carr
Inlet cadmium concentration. This value is within the overall range of
cadmium concentrations observed in Carr Inlet, however, and would not be
considered as evidence of elevated cadmium bioaccumulation in St. Paul
Waterway.
Lead and mercury data for crabs indicate possible elevation of tissue
concentrations in the waterways. The lead concentrations in crabs from
Sitcum and City Waterways were about 4.6 and 2.6 times higher, respectively,
than the Carr Inlet values (Table 3.37). Maximum lead concentrations in
these two areas (City, 1.65 mg/kg wet weight; Sitcum, 2.05 mg/kg dry weight)
were well above the range observed in Carr Inlet (0.14-0.35 mg/kg wet weight).
Although only one crab sample was collected from Hylebos Waterway,
its mercury concentration (0.220 mg/kg wet weight) was about five times
the average concentration measured in Carr Inlet samples. It should be
noted that maximum mercury concentrations in Milwaukee and Sitcum Water-
ways also exceeded 0.2 mg/kg wet weight.
3.6.4 Organic Compounds in Fish Muscle
Of the 100 U.S. EPA organic priority pollutants analyzed for, 84 were
not detected in any of the English sole or crab samples analyzed. A list
of the undetected compounds and their analytical detection limits is presented
in Table 3.38.
Although high molecular weight PAH (HPAH) occurred in sediments of
some waterways at concentrations up to 1,000 times beyond reference concen-
trations,HPAH were not detected in any of the 85 fish muscle tissue samples.
Detection limits for HPAH were typically 10 ug/kg wet weight. The absence
of these compounds in fish tissue is expected due to their rapid metabolism
by the mixed-function-oxidase system. PAH metabolites were not analyzed
as part of this study. However, available evidence indicates that HPAH
3.174
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Ul
TABLE 3.37. MEAN CONCENTRATIONS (mg/kg WET WEIGHT) OF
INORGANIC SUBSTANCES IN CRAB MUSCLE TISSUE
Species^ n
Carr Inlet
Hylebos Waterway
Blair Waterway
Site urn Waterway
Milwaukee Waterway
St. Paul Waterway
Middle Waterway
City Waterway
R
R
D
D
D
R
M
M
7
1
1
4
5
1
2
5
Arsenic
2.4
2.0
1.2
2.1
1.3
1.5
1.9
2.9
Cadmium
0.148
0.015
0.092
0.048
<0.013
0.620
0.175
0.083
Chromium
<0.24b
0.26
0.22
0.26
U0.14
0.25
0.25
0.22
Copper Lead
8.1
9.1
4.9
8.3
7.9
6.1
9.0
7.2
<0.20
0.23
0.18
0.93
0.31
0.14
0.32
0.53
Nickel
<0.107
0.220
U0.076C
U0.075
U0.075
U0.075
<0.127
U0.075
Silver
0.197
0.028
0.130
0.139
0.160
0.073
0.129
0.157
Zinc
47.4
44.0
43.0
37.7
36.2
36.0
42.0
43.8
Mercury
<0.045
0.220
U0.040
0.167
<0.110
U0.040
<0.050
0.068
a Species: D = Dungeness crab, R - rock crab, M = mixed species.
b U = Undetected in at least one sample. Detection limit used in calculation
of mean.
c U = Undetected at the detection limit shown.
-------
TABLE 3.38. U.S. EPA PRIORITY POLLUTANTS NOT DETECTED IN
ANY FISH OR CRAB MUSCLE TISSUE SAMPLE AT ANY OF 17 TRAWL TRANSECTS
Phenols (acids; 2 of 2) Typical Detection Limit3
phenol U 20
2,4-dimethylphenol U 20
Substituted Phenols (acids; 8 of 9)
2,4,6-trichlorophenol U 20
p-chloro-m-cresol U 20
2-chlorophenol U 20
2,4-dichlorophenol U 20
2-nitrophenol U 20
4-nitrophenol U 100
2,4-dinitrophenol U 100
4,6-dinitro-2-methylphenol U 25
Low Molecular Weight Aromatic Hydrocarbons (neutrals; 5 of 6)
acenaphthene U 10
acenaphthylene U 10
anthracene U 10
phenanthrene U 10°
fluorene U 10
High Molecular Weight PAH (neutrals; 10 of 10)
fluoranthene U
benzo(a)anthracene U 10
benzo(a)pyrene U 10
benzo(b)fluoranthene U 10
benzo(k)fluoranthene U 10
chrysene U 10
benzo(g,h,i)perylene U 10
dibenzo(a,h)anthracene U 10
indeno(l,2,3-c,d)pyrene U 10
pyrene U 10
Chlorinated Aromatic Hydrocarbons (neutrals; 4 of 6)
1,2,4-trichlorobenzene U 20
2-chloronaphthalene U 10
1,2-dichlorobenzene U 20
1,4-dichlorobenzene U 20
Chlorinated Aliphatic Hydrocarbons (neutrals; 2 of 3)
hexachloroethane U 40
hexachlorocyclopentadiene N/A
3.176
-------
TABLE 3.38. (Continued)
Halogenated Ethers (neutrals; 5 of 5)
bis(2-chloroethyl)ether U 20
4-chlorophenylphenylether U 20
4-bromophenylphenylether U 20
bis(2-chloroisopropyl)ether U 20
bis(2-chloroethoxy)methane U 20
Miscellaneous oxygenated compounds (neutrals; 2 of 2)
2,3,7,8-tetrachlorodibenzo-p-dioxin N/A
isophorone (3,5,5-trimethyl-2- U 10
cyclohexene-1-one)
Organonitrogen Compounds (bases; 8 of 8)
benzidine (4,4'-diaminobiphenyl) N/A
3,3'-dichlorobenzidine N/A
2,4-dinitrotoluene U 20
2,6-dinitrotoluene U 20
1,2-diphenylhydrazine (hydrazobenzene) U 10
nitrobenzene U 20
n-nitrosodiphenylamine U 10
n-nitrosodipropylamine U 20
Pesticides (neutrals; 18 of 18)
aldrin U 50
dieldrin U 50
chlordane U 50
4,4'-DDT U 50
4,4'-DDE U 50
4,4'-DDD U 50
alpha-endosulfan U 50
beta-endosulfan U 50
endosulfan sulfate U 50
endrin U 50
endrin aldehyde U 50
heptachlor U 50
heptachlor epoxide U 50
alpha-HCH U 50
beta-HCH U 50
delta-HCH U 50
gamma-HCH U 50
toxaphene (camphechlor) U 50
3.177
-------
TABLE 3.38. (Continued)
Volatile Halogenated Alkanes (neutrals; 16 of
carbon tetrachloride
1,2-dichloroethane
1,1,1-trichloroethane
1,1-dichloroethane
1,1,2-trichloroethane
1 , 1 ,2,2-tetrachl oroethane
chloroethane
chloroform
1 ,2-dichloropropane
methylene chloride (dichloromethane)
chloromethane
bromomethane
bromoform
bromodichloromethane
dichlorodifluoromethane
ch 1 orod ibromomethane
17)
U
U
U
U
U
U
U
U
U
NR
U
U
U
U
U
U
5
10
5
5
5
5
10
5
10
10
10
10
10
IOC
5
Volatile Halogenated Alkenes (neutrals; 5 of 6)
1,1-dichloroethene U 10
trans-l,2-dichloroethene U 5
cis and trans-l,3-dichloropropene U 10
trichloroethene U 5
vinyl chloride U 10
Volatile Aromatic Hydrocarbons (neutrals; 1 of 3)
benzene U 5
Volatile Chlorinated Aromatic Hydrocarbons (neutrals; 1)
chlorobenzene U 5
Volatile Unsaturated Carbonyl Compounds (base/neutrals; 2)
acrolein (an unsaturated aldehyde) U 100
acrylonitrile (an unsaturated nitrile) U 100
Volatile Ethers (neutrals; 2)
2-chloroethylvinyl ether U 100
a U = Undetected at the detection limit stated (ug/kg or ppb wet weight tissue)
NR = Not reported or all data rejected during QA review.
N/A = Not analyzed.
D Detected at <50 ppb in a single crab at MD-70C.
c Removed from priority pollutant list.
3.178
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metabolites are present primarily in the liver and bile, which are the
primary sites of metabolism and excretion (Stein et al. 1984).
Sixteen organic compounds were detected in one or more tissue samples.
Of this group, several phthalate esters (dimethyl phthalate, diethyl phthalate,
butylbenzyl phthalate) and volatile compounds (toluene and fluorotrichloro-
methane) were detected in only a few samples at very low concentrations
and were therefore not subjected to detailed analyses. The following 11
organic compounds were detected at sufficient frequencies and concentration
to be subjected to statistical evaluation: tetrachloroethene, ethylbenzene,
hexachlorobenzene, 1,3-dichlorobenzene, hexachlorobutadiene, naphthalene,
bis(Z-ethylhexyl) phthalate, di-n-butyl phthalate, di-n-octyl phthalate,
DDE, and total PCBs.
Muscle tissue concentrations of the most commonly detected organic
compounds in English sole are presented in Table 3.39. Average concentrations
of organic compounds by study area (i.e., waterways, Ruston-Pt. Defiance
Shoreline and Carr Inlet) are presented in Figures 3.61-3.67. Statistical
analyses of muscle tissue data indicated that only four compounds had signifi-
cant differences (P<0.05) in Commencement Bay study areas when compared
to the Carr Inlet reference area: naphthalene, bis(Z-ethylhexyl) phthalate,
di-n-butyl phthalate, and total PCBs. Concentrations of organic compounds
in English sole muscle tissue are compared by study area in the following
paragraphs.
Although several low molecular weight chlorinated compounds were detected
in fish muscle tissue, most of these compounds displayed very discontinuous
distributions, with only a few detected values. Hexachlorobenzene and
hexachlorobutadiene were detected in only two fish from Station HY-72 in
Hylebos Waterway. In both cases, these compounds were detected near or
below the normal detection limit. The mean concentrations of hexachloro-
butadiene and hexachlorobenzene in Hylebos Waterway were very similar to
those in other Commencement Bay locations or in the reference area (Figure
3.61). It should be noted, however, that the mean concentrations are based
on the analytical detection limits. The actual levels of these two compounds
in those areas may have been considerably less than the detection limits.
Tetrachloroethene was detected in all four areas sampled for volatile
organic compounds (Figure 3.62). Highest muscle tissue concentrations
(mean of 80 ug/kg wet weight) were measured in Hylebos Waterway, where
this compound was detected in seven of the eight English sole sampled.
Lower tissue concentrations of tetrachloroethene were measured in St. Paul
and City Waterways. Although concentrations of this compound were over
an order of magnitude greater in Hylebos Waterway than in Carr Inlet, there
were no statistically significant differences among areas because of relatively
high variability and low sample sizes (i.e., only four fish per area for
volatile compounds).
Ethylbenzene, another volatile compound, showed a similar distribution
in that it was detected in six of the eight English sole sampled in Hylebos
Waterway. However, the mean concentration of ethylbenzene in Hylebos Waterway
English sole was only 17 ug/kg wet weight. Lower tissue concentrations
were measured in English sole from City and St. Paul Waterways. Ethylbenzene
3.179
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TABLE 3.39. CONCENTRATIONS (ug/kg wet weight) OF ORGANIC COMPOUNDS
IN ENGLISH SOLE MUSCLE TISSUE AT ALL 17 TRAWL TRANSECTS
Trawl
Transect
CR70
CR71
HY70
HY71
HY72
BL70
BL71
BL72
SI70
MI70
SP70
MD70
CI70
CI72
RS70
RS71
RS72
1,3-Dichloro
benzene
U 20*
U 20
U 20
U 20
U 20
U 20
U 20
U 20
<66
U 20-250
U 20
U 20
U 20
<54
U 20-190
<134
U 20-530
U 24
U 20-U 40
U 20
U 20
Naphthalene
U 10
<98
U 10-320
U 10
U 10
<88
U 10-160
<30
U 10-110
<27
U 10-95
U 10
<18
U 10-84
<1,364
U 10-2.100
U 10
U 10
<64
U 10-210
<381
U 10-1,800
U 10
U 10
U 10
Total
PCB
<40b.c
U 20-60d
<32
U 20-40
536
70-1,300
300
60-500
159
65-310
<276
U 20-580
236
130-490
248
130-400
172
50-540
100
30-200
40
20-70
170
40-270
470
160-670
238
90-540
107
30-220
58
30-100
40
20-80
Di-n-butyl
Phthalate
U 10
<32
U 10-120
1,584
720-2,500
3,120
1,600-4,000
<22
U 10-70
<1 ,035
U 10-3,200
128
10-600
U 10
U 10
<70
U 10-310
U 10
U 10
4J 10
U 10
332
U 10-1,300
U 10
U 10
Bis(2-
ethylhexyl)
Phthalate
<60
U 10-Z260*
U 10
<52
U 10-220
<42
U 10-170
U 10
394
190-690
334
190-460
541
265-810
U 10
182
100-220
U 10
U 10
<482
U 10-980
70
10-310
<508
U 10-2,100
<30
U 10-110
<228
U 10-1,100
8 U = Undetected at the detection limit shown.
b < = Undetected in at least one sample. Detection limit used to calculate mean.
c Mean concentration.
d Range.
e Z - Value corrected for blank contributions.
3.180
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HEXACHLOROBUTADIENE
LU
tD
I5
"B)
a.
100 -i
80-i
60 -
40 -
20-
HY BL SI Ml SP MD Cl RS
CR
u>
•
•—•
00
g
LU
LU
D)
100-1
80-
60-
40-
20-
HEXACHLOROBENZENE
HY BL SI Ml SP MD Cl RS
CR
COMPOUND UNDETECTED IN ALL SAMPLES
Figure 3.61. Concentrations of hexachlorobutadiene and hexachlorobenzene in English
sole muscle tissue.
-------
TETRACHLOROETHYLENE
100 -|
00
ro
O
III
UJ
O)
—
-
••
;. • '*•• • .
• • •:; '
....; ..
, ,
HY
SP
Cl
CR
Figure 3.62. Concentrations of tetrachloroethylene in English sole muscle tissue.
-------
PENTACHLOROPHENOL
h-
g
in
LD
O)
m
O)
3.
100 -i
80-
60 -
40-
20 -
HY BL SI Ml SP MD Cl RS
CR
00
CJ
LU
tn
S1
O)
3.
100
80-
60
40
20
0
1,3-DICHLOROBENZENE
HY BL
SI
Ml SP MD Cl
RS
COMPOUND UNDETECTED IN ALL SAMPLES
CR
Figure 3.63. Concentrations of pentachlorophenol and 1,3-dichlorobenzene in English
sole muscle tissue.
-------
NAPHTHALENE
1400 -i
1300-
1200-
X
o
111
UJ
0) 300
200-
100 -
HY BL SI Ml SP MD Cl RS
CR
* AREAS SIGNIFICANTLY DIFFERENT FROM REFERENCE (P<0.05)
[~~| COMPOUND UNDETECTED IN ALL SAMPLES
Figure 3.64.
Concentrations of naphthalene in English sole
muscle tissue.
3.184
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DI-N-BUTYL PHTHALATE
00
en
X
o
LU
H
1600-1
1500-
400-
300-
200-
100-
HY BL SI Ml SP MD Cl RS
CR
D
# AREAS SIGNIFICANTLY DIFFERENT FROM REFERENCE (P<0.05)
COMPOUND UNDETECTED IN ALL SAMPLES
Figure 3.65. Concentrations of di-n-butyl phthalate in English sole muscle tissue.
-------
BIS(2-ETHYLHEXYL)PHTHALATE
00
01
500—1
400-
O
UJ 300-
111
200-
100 —
HY BL SI Ml SP MD Cl RS
CR
* AREAS SIGNIFICANTLY DIFFERENT FROM REFERENCE (P<0.05)
I""") COMPOUND UNDETECTED IN ALL SAMPLES
Figure 3.66. Concentrations of bis(2-ethylhexy1) phthalate in English sole muscle
tissue.
-------
TOTAL POLYCHLORINATED BIPHENYLS (PCB)
400 —
00
--J
300 -1
h-
o
ID
1- 200
LU
100 -
HY BL SI Ml SP MD Cl RS
CR
* AREAS SIGNIFICANTLY DIFFERENT FROM REFERENCE (P<0.05)
Figure 3.67. Concentrations of total PCBs in English sole muscle tissue.
-------
was not detected in English sole from Carr Inlet at a detection limit of
5 ug/kg wet weight.
1,3-Dichlorobenzene was detected only in fish from City and Sitcum
Waterways. Although this compound occurred at concentrations up to 530 ug/kg
wet weight in City Waterway, its detection was limited to 3 of 10 fish
in that area. Thus, the average tissue concentration in City Waterway
was only about five times the reference value (Figure 3.63).
Pentachlorophenol was detected in only one fish from Blair Waterway
at a concentration of 480 ug/kg wet weight. In all other samples, detection
limits ranged from 40 to 80 ug/kg wet weight.
Naphthalene was the only aromatic hydrocarbon detected in English
sole muscle tissue. Detection limits for aromatic hydrocarbons were typically
10 ug/kg wet weight. Naphthalene was not detected in English sole muscle
samples from Ruston-Pt. Defiance Shoreline, St. Paul Waterway, or Middle
Waterway. Relatively low average tissue concentrations (<50 ug/kg wet
weight) were measured in Hylebos, Blair, and Sitcum Waterways, and in Carr
Inlet. Most of the fish from these areas had no detected naphthalene,
with occasional fish having measured concentrations of 100-300 ug/kg wet
weight.
The highest average naphthalene concentration (1,300 ug/kg wet weight)
was measured in English sole from Milwaukee Waterway (Figure 3.64). Four
of the five fish from this waterway had naphthalene concentrations of 1,000-
2,100 ug/kg wet weight. Statistical analyses revealed that the Milwaukee
Waterway sole had significantly (PO.05) elevated naphthalene levels when
compared with Carr Inlet samples. None of the other study areas were signifi-
cantly (P>0.05) different from Carr Inlet.
The average naphthalene concentration in English sole from City Waterway
was 220 ug/kg wet weight. These sample results are not statistically sig-
nificant because only 2 of the 10 fish sampled displayed elevated naphthalene
concentrations (>75 ug/kg wet weight). Naphthalene was undetected in 4
of the 10 fish from City Waterway.
No pesticides were detected using 6C/MS in fish muscle tissue samples
from the study areas (Table 3.38). GC/MS detection limits for pesticides
were typically 50 ug/kg wet weight.
Because of previously documented pesticide contamination of sediments
and organism tissues in Commencement Bay, fish muscle samples were also
analyzed by GC/EC to measure pesticide concentrations at lower detection
limits, typically ranging from 0.8 to 12 ug/kg wet weight. Pesticides
analyzed by GC/EC included: p,p'-DDE, p,p'-DDD, p,p'-DDT, hexachlorocyclo-
hexane (lindane), aldrin, and dieldrin.
Of the six pesticides analyzed by GC/EC, only DDE was detected in
any of the English sole muscle samples. Average DDE concentrations in
Commencement Bay study areas ranged from 3.0 to 11.2 ug/kg wet weight (Table
3.40). Highest concentrations were measured in fish from Hylebos and City
Waterways, with maximum values of 30 and 24 ug/kg wet weight, respectively.
Although the tissue concentrations of DDE were relatively low throughout
3.188
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TABLE 3.40. CONCENTRATIONS OF p,p'-DDE IN
ENGLISH SOLE MUSCLE TISSUE
Concentration (ug/kg wet weight)
Area Mean Range
Carr Inlet
Hylebos Waterway
Blair Waterway
Sitcum Waterway
Milwaukee Waterway
St. Paul Waterway
Middle Waterway
City Waterway
Ruston-Pt. Defiance
Shorel ine
<1.8
<6.8b
9.2b
6.0
6.1
<3.0
3.1
11. 2b
<5.3
U 0.8-3.99
0.9-30
1.0-18
1.6-16
1.9-12
1.0-U 8.0
1.3-4.2
1.7-24
U 1.0-19
a U = Undetected at detection limit indicated.
b Significantly different from Carr Inlet, P<0.05 experi-
mentwise error rate.
3.189
-------
the study area, statistical analyses revealed significant elevations (PO.05)
in Hylebos, Blair, and City Waterways. Four of the Hylebos tissue samples
had relatively high DDE detection limits of 8.0 ug/kg wet weight. Removal
of these values from the Hylebos sample reduced the mean DDE concentration
to 6.4 ug/kg wet weight and eliminated the statistical significance for
Hylebos Waterway.
All six phthalate esters were detected in one or more of the English
sole muscle tissue samples. Concentrations of four phthalates (di-n-octyl,
dimethyl, diethyl, and butyl benzyl) were relatively homogeneous among
sampling sites, and none of the Commencement Bay areas were significantly
(P>0.05) different from Carr Inlet.
The remaining two phthalates [di-n-butyl and bis(2-ethylhexyl)] displayed
statistically significant (P<0.05) differences among sampling sites, but
their occurrences were highly dissimilar. Di-n-butyl phthalate was detected
in fish from Hylebos, Blair, and Milwaukee Waterways, the Ruston-Pt. Defiance
Shoreline, and Carr Inlet (Figure 3.65). Of these areas, only Hylebos
Waterway (mean concentration of 1,575 ug/kg wet weight) was significantly
(P<0.05) different from Carr Inlet. However, some fish from both Hylebos
and Blair Waterways contained relatively high concentrations of this compound
(maximum of 4,000 ug/kg wet weight). Di-n-butyl phthalate was also most
prevalent in Hylebos Waterway, where it was detected in 11 of the 15 English
sole sampled. The average concentration in Blair Waterway English sole
muscle tissue was less than that in Hylebos Waterway, and it was detected
in only 4 of 15 fish.
Bis(2-ethylhexyl) phthalate was detected in Blair, Milwaukee, and
City Waterways, the Ruston-Pt. Defiance Shoreline, and Carr Inlet (Figure
3.66). This compound was noticeably absent in fish from Hylebos Waterway.
Statistical analyses indicated that fish from Blair and Milwaukee Waterways
had significantly elevated muscle tissue concentrations when compared with
those from Carr Inlet. Highest concentrations of bis(2-ethylhexyl) phthalate
were measured in Blair Waterway (mean of 423 ug/kg wet weight), where all
15 fish sampled had detectable levels. The compound was detected less
frequently in the other areas.
Polychlorinated biphenyls (PCBs) were the most frequently detected
organic compound in samples of English sole muscle tissue. At a detection
limit of 20 ug/kg wet weight, 81 of the 85 fish analyzed had detectable
levels of PCBs. The prevalence of these compounds also enabled clear statis-
tical separation of study areas based on fish muscle concentrations.
PCBs were detected at relatively low levels (30-60 ug/kg wet weight)
in 7 of the 10 English sole from Carr Inlet. For the remaining three fish
from Carr Inlet, PCBs were undetected at 20 ug/kg wet weight. Statistical
comparisons of Carr Inlet with Commencement Bay areas indicated that sole
from Hylebos, Blair, Sitcum, and City Waterways had significantly elevated
muscle concentrations of PCBs (Figure 3.67). Evaluation of geographic
trends indicated that highest PCB concentrations occurred in sole from
Hylebos and City Waterways. Lowest levels were measured in intermediate
areas, especially Milwaukee and St. Paul Waterways. Fish collected along
the Ruston-Pt. Defiance Shoreline also had relatively low PCB levels.
3.190
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English sole from Hylebos Waterway had an overall average PCB concentration
of 332 ug/kg wet weight. This tissue level is approximately an order of
magnitude higher than that measured in Carr Inlet. There was considerable
variability, however, in PCB concentrations among English sole from Hylebos
Waterway (range of 60-1,300 ug/kg wet weight). The maximum PCB level for
Hylebos Waterway fish was also the highest concentration observed for the
study. Moreover, no other fish muscle samples contained more than
800 ug/kg wet weight of PCBs.
Within Hylebos Waterway, there appeared to be a gradient of declining
PCB concentrations in English sole from the waterway head to the mouth. This
apparent gradient was not statistically distinguishable, however. It should
also be noted that even at the uppermost Hylebos trawl site (HY70), two
of the five fish had muscle PCB concentrations of less than 100 ug/kg wet
weight.
English sole from City Waterway were more consistently elevated in
muscle PCB concentrations than those from Hylebos Waterway. The average
concentration in City Waterway samples was 354 ug/kg wet weight, with 9
of the 10 fish exceeding 150 ug/kg wet weight. English sole collected
near the head of City Waterway (CI70) also had higher PCB levels than sole
collected near the waterway mouth (Trawl Transect CI72).
English sole collected near the Old Tacoma fishing pier (Trawl Transect
RS70) had PCB levels of 30-220 ug/kg wet weight. PCB concentrations in
fish muscle tissue appeared to decline with proximity to Pt. Defiance.
PCB concentrations in English sole collected from the Pt. Defiance trawl
transect (RS72) were only 20-80 ug/kg wet weight, and were indistinguish-
able from the tissue levels measured in Carr Inlet.
Hydrophobic organic compounds such as PCBs tend to be associated with
the lipid fractions of organism tissues. Measured tissue concentrations
of organic contaminants can therefore be highly influenced by the amount
of lipid material in the sample. To evaluate whether or not observed dif-
ferences in tissue contaminant levels resulted from differences in lipid
content, the fish tissue data were re-evaluated based on the lipid content,
as measured by total extractable organic material. Overall, concentrations
of extractable organic material in English sole muscle ranged from 1.0
to 6.5 percent (Table 3.41). Average concentrations were relatively consistent
among study areas, however, and ranged from 2.1 to 3.1 percent. None of
the English sole muscle samples from Commencement Bay had significantly
different (P>0.05) lipid levels than samples from Carr Inlet.
To further evaluate the influence of lipids on organic priority pollutant
levels, the individual pollutant concentrations for each sample were normalized
to the mass of extractable organic materials. Lipid-normalized concentrations
were then subjected to statistical analyses to evaluate differences among
study areas. These analyses showed overall patterns similar to those resulting
from analyses of uncorrected concentrations, although several noticeable
differences existed. Reanalysis of the lipid-normalized data did not reveal
a statistically significant (P>0.05) increase in naphthalene concentrations
in English sole from Milwaukee Waterway, although the elevations above
reference for non-1ipid-normalized (24 times) and lipid-normalized (26
times) naphthalene levels were similar. As was the case for non-normalized
3.191
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TABLE 3.41. TOTAL EXTRACTABLE ORGANIC MATERIAL IN
ENGLISH SOLE MUSCLE TISSUE
Total Extractable
Organic Material (percent)
Area
Hylebos Waterway
Blair Waterway
Sitcum Waterway
Milwaukee Waterway
St. Paul Waterway
Middle Waterway
City Waterway
Ruston-Pt. Defiance
Mean
3.0
2.3
3.1
2.6
2.4
2.5
2.1
3.2
Range
2.2-6.5
1.5-3.7
2.2-4.1
2.4-2.8
1.4-3.2
1.9-3.2
1.0-2.8
1.9-5.7
Shoreline
Carr Inlet 2.5 1.9-3.8
3.192
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data, naphthalene levels in four of the five English sole from Milwaukee
Waterway considerably exceeded the range of concentrations measured at
Carr Inlet. Therefore, the 1ipid-normalized naphthalene data suggest con-
siderably elevated levels in Milwaukee Waterway fish. The lack of statistical
significance results from the relatively low sensitivity of the nonparametric
Mann-Whitney U-test to detect differences when the number of tied values
is decreased (as was the case for lipid-normalized data).
Statistical analysis of both lipid-normalized and non-1ipid-normalized
data for PCBs and bis(2-ethylhexyl) phthalate indicated some differences
between the two data sets. The differences in PCB concentrations between
samples from Sitcum Waterway and Carr Inlet were only marginally significant
in the non-normalized results, but not significant in the lipid-normalized
results. Therefore, the apparent elevation in PCB levels may result from
the high lipid content of Sitcum Waterway fish. PCB levels in English
sole from Hylebos, Blair, and City Waterways were significantly elevated
relative to Carr Inlet samples for both data sets. Fish from Milwaukee
Waterway did not display significantly (P>0.05) elevated lipid-normalized
levels of bis(2-ethylhexyl) phthalate. However, English sole from City
Waterway had statistically higher concentrations of lipid-normalized bis(2-ethyl-
hexyl) phthalate than did reference fish. This difference was not detected
in analysis of non-1 ipid-normalized data. In summary, analyses of lipid-
normalized tissue contaminant data revealed only one case [bis(2ethylhexyl)
phthalate] in which a statistically significant (P<0.05) elevation relative
to the reference value was observed that was not also detected in the non-
normalized data. The significant PCB elevations for both nornalized and
non-normalized data in fish from Hylebos, Blair, and City Waterways indicates
that these elevations are not due to sampling of fish with higher lipid
contents.
Ages of English sole used for bioaccumulation studies ranged from
3 to 10 yr. Because of the variability in fish age, an evaluation was
conducted to determine whether differences in tissue contaminant levels
among areas would result from differences in the age composition of English
sole samples.
The age composition of the English sole samples by area is presented
in Table 3.42. The mean age of English sole samples was relatively consistent
among study areas, and ranged from 5.0 to 6.3yr. Overall, English sole
used for tissue analyses ranged from 3 to 10 yr of age. Analysis of variance
of these data indicated no significant (P=0.549) differences among the
mean ages of English sole from the study areas identified in Table 3.42.
It is especially important to note that the mean age of the Carr Inlet
reference sample (5.7 yr) was very similar to the overall mean age (5.5 yr).
Therefore, there is no evidence that the observed differences in tissue
contaminant levels in English sole resulted from different age composition
of the samples.
3.6.5 Organic Compounds in Crab Muscle
Only six organic compounds were detected in samples of crab muscle
tissue. The detected compounds included two low molecular weight aromatic
hydrocarbons (phenanthrene and naphthalene), one high molecular weight
aromatic hydrocarbon (fluoranthene), three phthalate esters [bis(2-ethylhexyl),
3.193
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TABLE 3.42. AGE COMPOSITION OF ENGLISH SOLE SAMPLES
USED FOR BIOACCUMULATION ANALYSES
Study Area
Hylebos Waterway
Blair Waterway
Site urn Waterway
Milwaukee Waterway
St. Paul Waterway
Middle Waterway
City Waterway
Ruston-Pt. Defiance
Shoreline
Carr Inlet
All areas
Mean Age
5.1
6.3
5.6
5.0
5.2
5.3
5.0
5.5
5.7
5.5
Range
3-7
4-10
4-7
4-6
4-6
3-7
4-8
3-8
3-8
3-10
3.194
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di-n-butyl, and di-n-octyl phthalates], and PCBs. Phenanthrene and fluoranthene
were detected only in Middle Waterway crabs at low concentrations (29 and
48 ug/kg wet weight, respectively) and will not be discussed further.
Similarly, di-n-octyl phthalate was detected at low levels in Carr Inlet
crab samples only. Average concentrations of the remaining phthalate esters,
naphthalene, and PCBs are presented in Table 3.43.
In crab muscle samples, highest concentrations of naphthalene (1,200 ug/kg
wet weight) were measured in Milwaukee Waterway, a pattern similar to that
in English sole. However, naphthalene was only detected in one of the
five crabs analyzed from Milwaukee Waterway.
Bis(2-ethylhexyl) phthalate and di-n-butyl phthalate were both detected
at relatively high concentrations in the Carr Inlet crab samples (Table 3.43).
The only possible evidence of elevated phthalate levels in crab tissue
is for di-n-butyl phthalate in Hylebos Waterway. The presence of high
levels of this compound in Hylebos Waterway is consistent with the English
sole data.
PCBs were detected in crab tissue samples from all study areas except
for a single crab sample from Hylebos Waterway. However, it should be
noted that the analytical detection limits were unusually high (120 ug/kg
wet weight) for the single Hylebos crab sample. Maximum PCB concentrations
in crabs were generally less than those measured in English sole. Average
PCB concentrations in waterway crabs ranged from 1 to 10 times Carr Inlet
values. Highest overall concentrations (mean of 232 ug/kg wet weight)
were measured in crabs from Sitcum Waterway. These samples were from four
large Dungeness crabs (of legal size for recreational catch) collected
near the head of the waterway. Because most of the other crabs collected
in the waterways were considerably smaller, the PCB concentrations in the
Sitcum Waterway crabs may be more representative of the range of PCB levels
in edible-size crabs.
3.6.6 Comparison with Other Studies
The only other major bioaccumulation study in Commencement Bay fishes
was done by Gahler et al. (1982). This study involved the collection of
92 fish and crab muscle tissue samples from four Commencement Bay locations
(i.e., Hylebos Waterway, City Waterway, Old Town Dock, and Pt. Defiance
Dock) and a reference site at Discovery Bay. Samples were analyzed for
the full suite of U.S. EPA priority pollutants. Test species varied among
sampling sites and included English sole, walleye pollock, greenling, Pacific
hake, Pacific cod, and several other flatfish. English sole were consistently
sampled by Gahler et al. (1982) at all five sites and can be directly compared
to the results of this study.
Evaluation of the Gahler et al. (1982) data indicates that tissue
levels of contaminants in English sole muscle were generally two to three
higher than contaminant levels in other species. Therefore, English sole
serve as a conservative model for potential bioaccumulation in other Commence-
ment Bay species and enable consistent comparisons among areas. Concentrations
of inorganic substances reported by Gahler et al.(1982) in English sole
muscle tissue are presented in Table 3.44. In general, only chromium and
nickel displayed tissue concentrations consistently greater than two times
3.195
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TABLE 3.43. CONCENTRATIONS (ug/kg wet weight) OF SELECTED
ORGANIC COMPOUNDS IN CRAB MUSCLE TISSUE
Area
Carr Inlet
Hylebos Waterway
Blair Waterway
Site urn Waterway
Milwaukee Waterway
St. Paul Waterway
Middle Waterway
City Waterway
Naphthalene
Ua 10
U 10
U 10
<20
U 10-25
<248
U 10-1,200
U 10
U 10
U 10
Bis(2-ethylhexyl)
Phthalate
-------
VO
TABLE 3.44. CONCENTRATIONS (mg/kg wet weight) OF METALS IN
COMMENCEMENT BAY ENGLISH SOLE MUSCLE TISSUE AS
DETERMINED BY GAHLER ET AL. (1982)
Hy 1 ebos
n=5
City
n=5
Old Town
Dock
n=3
Pt. Defiance
Dock
n=3
D1 scovery
Bay
n=3
Median
Mean
Maximum
Median
Mean
Maximum
Median
Mean
Maximum
Median
Mean
Maximum
Median
Mean
Maximum
As
4.1
4.9
7.3
4.5
5.1
8.6
3.2
2.9
3.4
7.9
8.6
14.6
3.6
3.2
4.1
Cd
0.008
0.008
0.011
<0.005
<0.005
<0.005
0.006
0.007
0.008
0.004
0.007
0.012
0.006
<0.006
0.008
Cr
0.15
0.23
0.62
0.24
0.31
0.64
0.13
0.14
0.15
0.22
0.28
0.41
0.07
0.06
0.07
Cu
0.26
0.28
0.31
0.27
0.32
0.50
0.40
0.38
0.40
0.42
0.39
0.49
0.40
0.42
0.44
Pb
0.21
0.25
0.36
0.32
0.32
0.45
0.55
0.58
0.69
0.72
3.9
10.4
0.46
0.46
0.61
Hg
0.03
0.03
0.04
0.03
0.04
0.09
0.02
0.03
0.04
0.03
0.03
0.03
0.04
0.04
0.05
N1
1.2
1.3
1.4
0.52
0.65
1.2
0.45
0.46
0.48
0.43
0.52
0.73
0.17
0.23
0.33
Zn
5.0
5.1
5.6
5.0
5.5
7.7
6.0
5.9
6.3
7.0
6.5
7.3
4.7
5.2
7.0
-------
the reference values. Arsenic was elevated in bottomfishes from the Pt.
Defiance Dock (2.7-4.0 times reference concentrations), but did not display
substantial elevations at the other sites. Gahler et al. (1982) also collected
limited samples of Dungeness crab muscle tissue from the study area. Chromium,
copper, and lead were elevated about two to five times reference concen-
trations, suggesting increased bioaccumulation of these metals in Hylebos
and City Waterways.
The possible low-level elevations of chromium, copper, and arsenic
at Commencement Bay sites sampled by Gahler et al. (1982) are not substantiated
by the results of the present study. Average arsenic levels in English
sole from the Ruston-Pt. Defiance Shoreline area (6.3 mg/kg wet weight)
were slightly less than those detected by Gahler et al. (1982) (8.6 mg/kg
wet weight). However, the ranges of values for both studies are similar,
and the combined results indicate no significant elevations in tissue arsenic
levels in fishes from Commencement Bay.
The Gahler et al. (1982) results indicate that chromium and nickel
tissue concentrations were about two to six times higher in some Commencement
Bay sites relative to Discovery Bay. These apparent elevations are not
supported by the results of the present study. Chromium and nickel concen-
trations in English sole muscle were very consistent among sampling areas.
Since the Gahler et al. (1982) results indicate only relatively minor elevations
of these metals, it is concluded that chromium and nickel are not elevated
in Commencement Bay fishes.
The organic pollutant bioaccumulation results of Gahler et al. (1982)
are similar to the results of this study in that relatively few contaminants
were consistently detected in fish muscle tissue. Compounds detected consist-
ently included PCBs, phthalates, and DDT residues. Similarities between
the results of Gahler et al. (1982) and this study include:
• Hexachlorobenzene and chlorinated ethyl enes were detected
only in Hylebos Waterway fishes.
• Highest PCB levels with similar maximum values were measured
in fish from City and Hylebos Waterways (Table 3.45).
• DDT residues were measured in low concentrations throughout
the study area.
• Phthalates were detected at several locations in the study
area.
• There was no evidence of excess accumulation of hexachlorobuta-
diene in fish muscle.
Major differences between the two studies include the detection by
Gahler et al. (1982) of higher hexachlorobenzene levels (up to 150 ug/kg
wet weight) in English sole from Hylebos Waterway. Gahler et al. (1982)
also detected low levels of DDT, DDE, and ODD in fish muscle, whereas this
study detected only the DDE form of the pesticide.
3.198
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TABLE 3.45. CONCENTRATIONS (ug/kg wet weight) OF PCBs AND
HEXACHLOROBENZENE IN FISH MUSCLE TISSUE IN HYLEBOS
AND CITY WATERWAYS AS DETERMINED BY 6AHLER ET AL. (1982)
PCB
Area
Hylebos Waterway
City Waterway
Old Town Dock
Pt. Defiance Dock
Fish Species
Whitespotted
green! ing
English sole
Pacific stag-
horn sculpin
English sole
Walleye pollock
Pacific cod
English sole
Pacific hake
Walleye pollock
English sole
Walleye pollock
Pacific staghorn
sculpin
Mean
860
550
260
190
170
37
120
93
24
330
58
49
Range
540-1,120
130-1,030
170-340
54-360
17-530
36-38
91-160
50-140
17-33
100-640
17-130
45-52
HCB
Mean Range
59 14-96
110 56-150
31 28-34
uai
U 1
U 1
U 1
U 1
U 1
U 1
U 1
U 1
U = Undetected at detection limit shown.
3.199
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Gahler et al. (1982) measured higher PCB levels in English sole from
the Ruston-Pt. Defiance Shoreline than were measured in this study. For
the samples collected in 1981, the muscle tissue concentrations of PCBs
in English sole from the Ruston-Pt. Defiance area ranged from 91 to 640 ug/kg
wet weight. For the present study, English sole collected in the same
area in 1984 had PCB levels of 20 to 100 ug/kg wet weight. The reasons
for these apparent differences are unknown.
Malins et al. (1982) reported PCB concentrations ranging from 160
to 850 ug/kg wet weight in English sole muscle samples from Commencement
Bay. The location and time of collection of these samples were not reported
by Malins et al. (1982), however. Since Malins et al. (1980, 1982) have
previously collected fish from Hylebos and City Waterways, it is assumed
that at least some of the five samples came from these areas and were probably
collected around 1981. The PCB values reported by Malins et al. (1982)
for English sole are within the range of values measured in the present
study for Hylebos and City Waterways.
3.6.7 Summary
• With the exception of copper, metal concentrations in English
sole muscle tissue were relatively homogeneous among study
areas. For these metals there was no evidence of excessive
accumulation in Commencement Bay fish when compared with
those from the Carr Inlet reference area. The maximum average
concentrations of most metals in Commencement Bay fish were
less than 2 times the average reference concentration.
Copper was significantly elevated (3-9 times reference)
in fish from several areas of Commencement Bay.
• The only metals displaying elevated concentrations in Commence-
ment Bay crabs were lead and mercury. Maximum elevations
of these metals in crab muscle were about five times reference
concentrations.
• There was no evidence of arsenic accumulation above reference
levels in fish or crabs from Commencement Bay.
9 Only 10 organic compounds were detected in more than a few
fish samples from Commencement Bay.
• The only aromatic hydrocarbon detected in English sole muscle
was naphthalene, which occurred at relatively high concentrations
in City and Milwaukee Waterways.
t The chlorinated compounds hexachlorobenzene and hexachloro-
butadiene were detected only at relatively low concentrations
(about 40 ug/kg wet weight) in two of five English sole
from a single Hylebos Waterway trawl.
• PCBs were detected in all fish sampled in Commencement Bay
and occurred at maximum concentrations (approximately 10
times reference) in English sole from Hylebos and City Waterways.
3.200
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The only pesticide detected in Commencement Bay sole was
DDE, which occurred at relatively low concentrations (generally
<10 ug/kg wet weight) throughout the study area.
PCBs were the only organic compounds consistently detected
in Commencement Bay crabs. PCB concentrations in crabs
were generally less than concentrations in English sole.
3.201
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4.0 CONTAMINANT, TOXICITY, AND BIOLOGICAL EFFECTS RELATIONSHIPS
4.1 INTRODUCTION
Quantitative relationships among the contaminant, toxicity, and biological
effects variables used in the Commencement Bay Superfund Investigation
are examined in this section. In Section 5, these variables are used
independently to assess environmental hazards and to prioritize study areas.
The data analyses conducted in Section 4 are designed to meet two objectives:
1. To determine levels of sediment contamination above which
significant toxicity or biological effects would be expected
to occur
2. To identify contaminants of concern from the numerous contami-
nants detected at elevated concentrations in Commencement
Bay sediments.
These objectives were met by evaluating whether there was increased
toxicity or biological effects with increasing sediment contaminant concentra-
tions. Both statistical and nonstatistical approaches were used to investigate
these relationships. The Commencement Bay database includes sediment chemistry
and biological information at sites displaying a wide range of sediment
contaminant levels. Therefore, these data were used to determine threshold
effect levels of contaminants or contaminant groups that could be used
to evaluate potential toxicity or biological effects at sites where only
sediment chemistry data were available.
For a given area (e.g., a waterway), these relationships will identify
the contaminants that seem to be most responsible for any observed toxicity
or biological effects. In this study, it was assumed that contaminants
displaying monotonically increasing relationships with a toxic or biological
effect had a higher relative priority (i.e., a higher potential for being
a causative agent) than contaminants displaying no discernible relationships
with effects.
This section also examines the interrelationships among some of the
important toxicity and biological variables (i.e., benthic infauna vs.
bioassays, and bioaccumulation vs. histopathology in English sole). The
objectives of these assessments are to evaluate the relative merits of
the independent biological measurements and to develop recommendations
for future use of these variables.
4.2 RELATIONSHIPS AMONG CONTAMINANTS, TOXICITY, AND BENTHIC EFFECTS
This section examines the correspondence among concentrations of sediment
contaminants and occurrences of significant sediment toxicity and benthic
effects (defined in Sections 3.2 and 3.3). Concentrations [dry-weight
(DW)] of at least one organic or inorganic contaminant were elevated above
Puget Sound reference conditions in surface sediments from all Commencement Bay
4.1
-------
stations. Significant toxicity or benthic effects were observed at 29 of
the 52 Conmencement Bay stations where bioassays and benthic infaunal studies
were conducted. Hence, elevated chemical concentrations did not always
result in statistically significant effects. Sources of variability associated
with contaminant-benthic infauna relationships included random variability
at each benthic station. Benthic sampling was conducted synoptically with
chemical sampling, but used different grab samples. This variability was
a smaller factor in contaminant-toxicity relationships because bioassays
were conducted on homogenized aliquots of the same sediment sample taken
for chemical analysis.
Toxicity and benthic "apparent effect thresholds" (AET) for chemical
contaminants are derived in this section by comparing the magnitudes of
chemical contamination between three groups of sediments: 1) sediments
that do not exhibit toxicity, 2) sediments that do not exhibit benthic
effects, and 3) sediments that do exhibit toxicity or benthic effects.
Chemicals with concentrations exceeding an AET are summarized for each
station where significant toxicity or benthic effects were observed.
Because of the wide variation in chemical composition among Commencement
Bay areas, it is unlikely that a single contaminant or group of contaminants
was associated with all observed toxicity or benthic effects. Therefore,
the spatial distributions of chemical concentrations exceeding an AET were
compared with gradients of sediment toxicity and benthic responses at closely
spaced stations. This comparison was used to determine which, if any,
chemical concentration gradients corresponded to toxicity or effects gradients
within small areas. Chemicals with concentrations that exceeded AET and
correlated with toxicity or benthic effects gradients at affected sites
received the highest priority for source evaluation in later sections.
4.2.1 Correlation of Indicators
Sediment toxicity was observed at 25 of 52 stations in Commencement
Bay study areas, as evidenced by statistically significant mortality in
the amphipod bioassay or abnormality in the oyster larvae bioassay. Significant
benthic effects were observed at 18 of the 50 stations sampled for benthic
infauna. Benthic effects were defined as a statistically significant depression
in the abundance of one or more major taxa relative to conditions at a
reference area with sediments of similar texture. Variations in the concen-
trations of sediment contaminants at biological stations were examined
to identify correspondence between contaminant concentrations and observed
toxicity or benthic effects. Because sediment characteristics (i.e., total
organic carbon, percent fine-grained material) may influence the toxic
response of organisms to a contaminant, relationships among sediment contami-
nation, sediment toxicity, and benthic effects were evaluated using contaminant
concentrations normalized alternatively to sediment dry weight, total organic
carbon, and percent fine-grained material.
Where synoptic biological and chemical data were collected, significant
toxicity in both bioassays as well as benthic effects were observed at
all but one station where the dry-weight concentration of at least one
metal or organic compound exceeded 1,000 times reference conditions (i.e.,
chemicals listed in Table 3.12 in Section 3.1.5.3). The exception was
Station HY-43, where trichlorinated butadiene concentrations were nearly
4.2
-------
2,000 times reference conditions, but neither bioassays nor benthic effects
were significant. In other sediments where there were no significant toxic
responses or benthic effects, concentrations of organic compounds (besides
chlorinated butadienes) ranged from 1 to <400 times reference conditions
and concentrations of metals were <50 times reference conditions.
Sediment toxicity and the number of significant benthic effects were
highest in the most chemically contaminated study areas. Toxicity increased
and abundances of major taxa decreased with increasing concentrations of
some contaminants over the entire study area. Examples of this relationship
are given in Figure 4.1. A common characteristic of these plots was con-
siderable scatter in the magnitude of sediment toxicity and taxa abundances
at lower chemical concentrations. When trends were observed, the minimum
toxicity increased and the maximum abundances decreased at higher contaminant
concentrations. When data from all study areas were plotted together for
a given contaminant, there was no clear trend in the values of maximum
toxicity or minimum abundances over the concentration range of the contaminant.
This latter feature is consistent with the conclusion that no one contaminant
or contaminant group correlated with the effects observed in all areas.
In some cases there was random scatter in the values up to a certain
contaminant concentration. Above that concentration, there was an rapid
change to uniformally high toxicity or low abundances at the few most
contaminated sites. If the high contaminant levels were associated with
the effects observed, the abrupt change in the scatter suggested an "effect
threshold" for the contaminant. These potential "effect thresholds" are
evaluated in the following section.
4.2.2 Apparent Chemical Effect Thresholds
The use of synoptic chemical, toxicity, and benthic infaunal data
in predicting concentrations of contaminants (e.g., lead) above which toxicity
and benthic effects would be expected is shown in Figure 4.2. Results
from all 52 Commencement Bay stations with concurrent chemical, toxicity,
and benthic data were used in this evaluation. Benthic infauna data were
not collected for two stations along the Ruston-Pt. Defiance Shoreline
(RS-22 and RS-24).
The range in lead concentrations (DW) at biological stations is shown
in Figure 4.2 for three groups of sediment samples. The first group consisted
of the 32 stations where no statistically significant benthic effects were
observed. The lead concentration for this "no benthic effects" group ranged
from 8.3 to 300 mg/kg DW. The second group consisted of the 28 stations
where no statistically significant sediment toxicity was observed in bioassays.
The lead concentration for this "no toxicity" group ranged from 8.3 to
660 mg/kg DW. The third group consisted of the 29 stations where either
statistically significant sediment toxicity or benthic effects were observed.
The lead concentration for this "affected" group of stations ranged from
11 to 6,250 mg/kg DW.
Some stations were included in more than one group. For example,
significant sediment toxicity was observed at 9 of the 32 stations that
exhibited no significant benthic effects. These nine stations were included
in both the "no benthic effects" group and in the "affected" group. Likewise,
4.3
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LEAD
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ELEVATION ABOVE REFERENCE
1X = 9.2 mg/kg DW 10X
| 1 i I i i i i il i
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11ppm
SOOppm
660ppm
6300ppm
r
10
,,,,,,,, .
100
CONCENTRATION
(mg/kg DW)
• APPARENT
POTENTIAL SCALE BENTHIC
EFFECT EFFECT
THRESHOLD THRESHOLD
i i i
, , ,,
1000
APPARENT
TOXICITY
THRESHOLD
T 10000
MAXIMUM
OBSERVED
i FX/FI AT A
BIOLOGICAL
STATION
Figure 4.2. Example use of synoptic benthic effects and sediment toxicity data to
determine apparent chemical effect thresholds.
-------
the 23 Commencement Bay stations where neither significant benthic effects
nor sediment toxicity were observed were included in both the "no benthic
effects" group and in the "no toxicity" group. The range of lead concentrations
for these 23 stations was 8.3 to 300 mg/kg DW.
The concentration range of lead for the "affected" group of sediments
indicated that significant sediment toxicity or benthic effects did not
occur at the Commencement Bay biological stations when lead levels were
below 11 mg/kg DW (EAR = 1.2). This level defined a "potential effect
threshold" (i.e., higher lead concentrations may have resulted in significant
sediment toxicity or benthic effects). This threshold was termed "potential"
because toxicity or benthic effects were found at some, but not all, of
the stations with higher lead concentrations. The toxicity or benthic
effects observed at these stations could have resulted from other contaminants
or conditions.
A toxicity "apparent effect threshold" (AET) was defined as the contaminant
concentration above which significant sediment toxicity would always be
expected (Figure 4.2). Similarly, benthic AET was defined at the contaminant
concentration above which significant benthic effects would always be expected.
The toxicity AET and benthic AET may or may not occur at the same concentration
of a chemical. For example, significant benthic depressions were observed
at all seven stations with lead concentrations greater than 300 mg/kg DW
(EAR = 33). Significant sediment toxicity was also observed at all three
stations with lead concentrations greater than 660 mg/kg DW (EAR = 72).
These effect thresholds were termed "apparent" because significant toxicity
or benthic effects were not found at some stations with equal or lower
lead concentrations, while significant sediment toxicity or benthic effects
were found at all stations with higher concentrations. These empirical
relationships do not prove that contaminants found above an AET were
responsible for the observed toxicity or benthic effects. Within the limits
of this data set, chemicals present above this concentration were associated
exclusively with problem sediments having significant toxicity or depressed
benthic infaunal abundances (or both). Because of this association, all
chemicals present above an AET were defined as problem chemicals requiring
further evaluation.
Major sources of variability in determining AET include: 1) the
statistical error (P<0.05) associated with the significance of bioassay
and benthic infauna results, and 2) the analytical error associated with
the quantification of chemical results. The analytical precision attained
typically ranged from 5 to 50 percent (relative percent difference) depending
on the chemical. The accuracy of the organic compound results was improved
by use of isotope dilution mass spectroscopy to provide a minimum correction
for compound recovery (see Methods Section 2.2).
The AET determined in this section do not distinguish potential synergism
and other factors that may contribute to observed toxicity or benthic effects
at one station but not at another. The contribution of these factors cannot
be determined from the data available. With the existing data, the approach
does provide a means of prioritizing the list of potential problem chemicals
by giving less weight to those for which contradictory evidence was found
at stations without significant toxicity or benthic effects.
4.6
-------
The approach shown in Figure 4.2 was used to identify toxicity and
benthic AET for all chemicals of concern summarized in Section 3.1 (see
Tables 3.4 and 3.10), in addition to tentatively identified organic compounds
detected at multiple sites (see Table 3.6). These AET expressed on a dry-
weight basis are summarized for metals and organic compounds in Tables 4.1
and 4.2. Where the observed effect threshold for sediment toxicity differed
from that for benthic effects, both AET are shown. Biological stations
where each contaminant exceeded either AET are also identified. Corresponding
AET for conventional variables (e.g., total organic carbon) are summarized
in Table 4.3.
One or more metals exceeded an AET in sediments from stations in Hylebos,
Sitcum, and City Waterways, and along the Ruston-Pt. Defiance Shoreline.
Several metals had different sediment toxicity and benthic effects thresholds.
Without exception, the AET was higher for sediment toxicity than for benthic
effects, suggesting that benthic effects were more sensitive to metals
than were bioassay responses.
One or more organic compounds or compound groups exceeded an AET at
stations in Hylebos, Sitcum, St. Paul, and City Waterways, and along the
Ruston-Pt. Defiance Shoreline. AET were usually higher for benthic effects
than for sediment toxicity where there were differences between these
indicators. These data suggest that bioassay responses were more sensitive
to organic compound contamination than were benthic effects.
Chemicals with concentrations that exceeded an AET (DW) at each of
the 29 stations exhibiting a significant toxic response or benthic effect
are summarized in Table 4.4. Concentrations of one or more metals exceeded
these levels at 41 percent (12/29) of the affected stations. Organic compounds
were found above an AET at 76 percent (22/29) of the stations. Wherever
sediment toxicity and benthic effects were observed together, at least
one chemical exceeded an AET (DW) . Likewise, wherever both amphipod and
oyster larvae biossay results were significant, some chemical exceeded
an AET, even when no significant benthic effects were observed.
No chemicals exceeded an AET (DW) at 21 percent (6/29) of the stations
exhibiting a significant toxic response or benthic effect. Four of these
six stations were unusual in that the only effect observed was significant
amphipod mortality. These four stations (B-15, BL-25, MI-11, and MI-15)
were the only stations with significantly toxic sediments of all biological
stations in Blair and Milwaukee Waterways. The mean amphipod mortality
at these four stations ranged from 20 to 32 percent. A common characteristic
among these stations was the presence of fine-grained material in excess
of 80 percent (82, 88, 86, and 85 percent, respectively). Sediment contami-
nation in both Blair and Milwaukee Waterways was relatively low compared
with other Commencement Bay areas. Moreover, no significant benthic effects
or oyster larvae abnormalities were observed at any biological station
in either waterway. These data suggest that the amphipod bioassay may
be responsive to high levels of fine-grained material in sediments in addition
to chemical contamination. Ott (1985) also found that Rhepoxinius abronius
in bioassays appear to respond negatively to high 1 eve!s of fine-grainecf
material. Alternative explanations for the patterns observed in Blair
and Milwaukee Waterways include:
4.7
-------
TABLE 4.1. APPARENT EFFECT THRESHOLDS FOR POTENTIAL PROBLEM
METALS NORMALIZED TO DRY WEIGHT
00
APPARENT
EFFECT
THRESHOLD
METALS (mg/kg)
Antimony 5.3/3.1
Arsenic 93/85
Cadmium 5.8
Copper 310
BIOLOGICAL STATIONS
AND CONCENTRATIONS
EXCEEDING THRESHOLD
(mg/kg)
RS-22
RS-24
RS-19
RS-18
HY-17
HY-22
RS-20
SI-11
RS-24
RS-19
RS-18
CI-13
RS-24
RS-19
RS-18
RS-24
RS-19
RS-18
5.3
26
36
420
86
90
90
93
700
1,500
9.700
6.7
9.6
16
180
390
2,200
11,000
APPARENT BIOLOGICAL STATIONS
EFFECT AND CONCENTRATIONS
THRESHOLD EXCEEDING THRESHOLD
METALS (mg/kg) (mg/kg)
Lead 660/300 CI-13
SI-12
RS-24
SI-11
CI-11
RS-19
RS-18
Mercury 0.59/0.52 CI-11
RS-20
CI-13
RS-19
RS-18
Nickel 39 CI-11
SP-14
HY-22
HY-23
RS-18
Z1nc 490/260 HY-17
CI-11
SI-12
SI-11
RS-19
RS-18
RS-24
450
500
530
660
720
1,000
6,300
0.53
0.59
1.1
3.2
52
40
40
52
56
93
270
320
340
490
910
3,300
1,600
a Where two values are shown, the one on left Is the toxldty threshold and the one on right Is the benthlc effects
threshold. The lower of these paired values 1s underlined. Where only one value Is shown, the two apparent
thresholds are Identical.
-------
TABLE 4.2. APPARENT EFFECT THRESHOLDS FOR POTENTIAL PROBLEM
ORGANIC COMPOUNDS NORMALIZED TO DRY WEIGHT
ORGANIC COMPOUNDS
Phenol
2-Methyl phenol
4-Methylphenol
LMU aromatic hydrocarbons
HMU aromatic hydrocarbons
Chlorinated benzenes
Chlorinated butadienes
Total phthalates
Total PCBs
Benzyl alcohol
APPARENT BIOLOGICAL STATIONS
EFFECT AND CONCENTRATIONS
THRESHOLD EXCEEDING THRESHOLD
(ug/kg) (ug/kg)
420/1, ZOO HY-12
HY-22
CI-11
CI-20
SP-14
63/72 RS-I8
RS-I3
670 SP-I6
CI-16
SP-15
SP-14
5,200 SP-14
RS-18
12.000/17.000 HY-14
HY-17
HY-22
RS-18
270/400 RS-18
HY-47
HY-42
CI-11
CI-16
HY-22
h f
47,000°iC NONE
3.400/5.200 CI-13
HY-22
HY-12
420/1,100 HY-42
HY-23
HY-22
130 SP-16
CI-11
500
530
1,100
1.200
1,700
71
71
890
1,200
2,600
96,000
6,100
20.000
17,000
18,000
30,000
31.000
290
310
400
430
680
1,300
3,600
3,700
5,200
1,100
1,500
2.000
130
140
ORGANIC COMPOUNDS
Olbenzofuran
Aniline
N-N1trosod1phenylam1ne
Tetrachloroethene
Ethylbenzene
Total xylenes
l-Methyl-2-(l-methyl-
ethyl) benzene6
2-Methoxy phenol*
l.l'-B1phenyl«
Dlbenzothlophene*
Pentachlorocycopentane*
Dlterpenold hydrocarbons
Isoplmardlene6
Unidentified f
d1terpenee>r
Retene6
APPARENT
EFFECT
THRESHOLD
(ug/kg)
540
U 20d
28
140
37
120
2.300/1.100
930
260/270
240/250
k f
72b.c
1,500
2,000
1.200/2.000
BIOLOGICAL STATIONS
AND CONCENTRATIONS
EXCEEDING THRESHOLD
(ug/kg)
RS-18
CI-11
RS-24
SI-12
CI-16
RS-18
HY-23
HY-17
HY-17
HY-17
SP-15
SI-11
HY-17
SP-14
SP-15
SP-14
CI-20
SP-14
RS-18
CI-20
HY-22
RS-18
NONE
SP-14
SI-12
SP-14
SP-16
SI-15
2,000
1,400
40
130
220
610
170
210
50
160
1,400
2,300
2,800
6.600
1,500
3.900
270
310
1.100
250
320
1,100
5,900
2,100
5,200
1.700
2,000
* Where two values are shown, the one on left Is the toxlclty threshold and the one on right Is the benthlc effects threshold. The lower of
these paired values 1s underlined. Where only one value 1s shown, the two apparent thresholds are Identical.
D No apparent toxlclty threshold was observed for this chemical. The value shown 1s the maximum concentration observed.
c No apparent benthlc effects threshold was observed for this chemical. The value shown Is the maximum concentration observed.
d Aniline was undetected at 20 ug/kg DW at all stations except CI-11.
• This compound was Identified by matching the sample spectra with library reference spectra. The Identification Is considered tentative
because standards of this compound are not routinely analyzed.
' Possibly kaur-16-ene.
-------
TABLE 4.3. APPARENT EFFECT THRESHOLDS FOR CONVENTIONAL VARIABLES
PARAMETER
APPARENT
EFFECT
THRESHOLD3
BIOLOGICAL STATIONS AND
CONCENTRATIONS EXCEEDING
THRESHOLD
Total volatile solids (%)
Total organic carbon (%)
Nitrogen (%)
Oil and yrease (my/kg)
22.2
lb.1
0.28
2.200/4.300
SP-14
SP-14
CI-13
CI-11
CI-16
SP-14
HY-47
SP-16
CI-16
Cl-13
RS-18
B-15
CI-11
44.7
16
0.29
0.3b
0.49
0.79
0.89
1.2
3,300
3,400
4,100
4,300
b,700
a Where two values are shown, the one on left 1s the toxIcUy threshold and the one
on right 1s the benthlc effects threshold. The lower of these paired values Is underlined.
Where only one value Is shown, the two apparent thresholds are Identical.
4.10
-------
TABLE 4.4. SUMMARY OF EFFECTS AND POTENTIAL PROBLEM CHEMICALS
AT BIOLOGICAL STATIONS (NORMALIZED TO DRY WEIGHT)
Toxic ity
and/or
Effect*
0
M
0 M C
0 A M C
0AM P T
M C T
M
A
0 M
A
A
C
A C
A
A
A
0
0 A M C P T
0 A M C
0 A T
0AM
0 M C P T
0 M C P T
0 A
0 A
0 A M C P T
0AM
M
Ae
Station
HY-12
HY-14
HY-17
HY-22
HY-23
HY-32
HY-37
HY-42
HY-47
B-15
BL-25
SI-11
SI-12
SI-15
MI-11
MI-15
SP-12
SP-14
SP-15
SP-16
CI-11
CI-13
CI-16
CI-20
RS-13
RS-18
RS-19
RS-20
RS-24
Chemical13 Exceeding An Apparent Effect Threshold
PNOLC, PHTH
HPAH
LPAH, PCE, XYL, EBEN, ASd, Znd, MBEN
PNOLC, HpAH, PHTHC, TPCB> CBEN, HCBD, Asd, Ni , DIB
HPAHd, TPCB> PCE, Ni
TPCB, CBENC, HCBD
CBENC, HCBD, N
0 & Gc
ASd, Pbd Znd MBENd
NDPA, Pba, Znd, DTPc
RETAC
4MNOL, PNOL, LPAH, Ni , MBEN, MOX, DTP, BIPH, TVS, TOC N
4MNOL, MBENb, MOX
4MNOL, BZOH, RETC, N
PNOLC, BZOH, ANIL, HPAHd, CBEN, Hgd, Pb, Ni , Znd, O&G, N, S
PHTHC, cd, Pbd, Hg, O&G, N, S
4MNOL, CBEN, NDPA, O&G, N, S
PNOLC, BIPHC, DIBC,
2MNOLC
2MNOL, NDPA, LPAH, HPAH, CBENC, BIPH, DIB, QBp, $b , As
Cd , Cu , Pb , Ah , Ni , Zn
Sb. As, Cd, Cu, Pb, Hg, Zn
Asa, Hgd
NDPA, Sb, As, Cd, Cu, Pbd, Zn
4.11
-------
TABLE 4.4. (Continued)
a 0 = oyster abnormality
A = amphipod mortality
M = mollusc abundance
C - crustacean abundance
P = polychaete abundance
T = total benthic abundance
D PNOL = phenol
HPAH = high molecular weight aromatic hydrocarbons
PCE = tetrachloroethene
XYL = total xylenes
EBEN = ethylbenzene
MBEN = 1-methyl-2-(methyl ethyl)benzene
PHTH = total phthalates
TPCB = total PCBs
CBEN = total chlorinated benzenes
HCBD = hexachlorobutadiene
MPYR = methylpyrene
MPHEN = methylphenanthrenes
DBF = dibenzofuran
NDPA = n-nitrosodiphenylamine
DTP = isopimaradiene (diterpene)
unidentified diterpene (possibly kaur-16-ene)
RET = retene
4MNOL = 4-methylphenol
2MNOL = 2-methyl phenol
LPAH = low molecular weight aromatic hydrocarbons
MOX = 2-methoxyphenol
BIPH = l.l'-biphenyl
TVS = total volatile solids
TOC = total organic carbon
BZOH = benzyl alcohol
ANIL = aniline
DIB = dibenzothiophene
O&G = oil and grease
Pb = lead
As = arsenic
Zn = zinc
Ni = nickel
Hg = mercury
Cd = cadmium
Sb = antimony
Cu = copper
N = total nitrogen
S = total sulfides
c Chemical exceeded apparent effect threshold for toxicity only.
d Chemical exceeded apparent effect threshold for benthic abundance only,
e No benthic abundance data available for RS-24.
4.12
-------
• The amphipod bioassay results from these stations may have
reflected synergistic or additive effects of chemicals present
at low concentrations relative to other Commencement Bay
sites.
t The bioassay response may have resulted from the presence
of some unmeasured chemical whose spatial distribution does
not covary with those of the over 150 chemicals measured
in this study.
Because there were no corroborative data from the oyster larvae bioassay
or any benthic indicator, these alternative explanations do not appear
as plausible as the grain size explanation. The only other occurrence
of a significant amphipod bioassay response in the absence of other toxicity
or benthic effect responses was at Station SI-15 at the mouth of Sitcum
Waterway (average mortality = 25 percent). This station also had a high
percentage of fine-grained material (81 percent), and retene (tentative
identification) was the only chemical elevated at this station above its
toxicity AET. Although chemical toxicity may be a factor at SI-15, it
is possible that the single bioassay response at these five stations reflects
grain size factors only. Sediment from four other biological stations
in the Commencement Bay studies had a fine-grained material content ranging
from 82 to 89 percent, yet did not exhibit significant amphipod mortality.
Therefore, if grain size factors do influence amphipod bioassay results,
a consistent pattern among all fine-grained sediments has not been demonstrated.
Significant oyster larvae abnormality was observed at two stations
where no other toxic or benthic response was found. One of these stations
(HY-12) had a high percentage of fine-grained material (78 percent), but
the other station did not (SP-12; 49 percent). Oyster larvae abnormalities
were generally higher in sediments with higher TOC levels (e.g., Figure 4.1).
This correspondence was not observed between amphipod mortality and TOC.
Sediments from Stations HY-12 and SP-12 were moderately enriched with organic
carbon (5.7 and 4.7 percent, respectively). This organic enrichment may
have been a factor in the oyster larvae results. There were no other
physicochemical factors consistent between these stations. No chemical
exceeded an AET (DW) at Station SP-12 (Table 4.4).
Significant benthic effects without sediment toxicity were observed
at four stations (Table 4.4). No chemical exceeded an AET (DW) at Stations
HY-32 or HY-37. The presence of multiple benthic depressions observed
at Station HY-32 was the only such occurrence in the absence of a significant
bioassay response. Stations SI-11 and RS-20 had a single significant depression
of Crustacea and Mollusca, respectively. In each case, the concentration
of at least one metal exceeded an AET (DW).
Toxicity and benthic AET for metals and organic compounds normalized
to the sediment organic carbon content are summarized in Tables 4.5 and 4.6.
A summary of chemicals with concentrations exceeding an AET normalized
to TOC at each of the 29 stations exhibiting a significant toxic response
or benthic effect is given in Table 4.7. Analogous results for chemicals
normalized to percent fine-grained material are given in Tables 4.8, 4.9,
and 4.10. The format of these tables and the approach used to determine
"apparent effect thresholds" were the same as for Tables 4.1, 4.2,, and 4.4.
4.13
-------
TABLE 4.5. APPARENT EFFECT THRESHOLDS FOR POTENTIAL
PROBLEM METALS NORMALIZED TO ORGANIC CARBON
APPARENT
EFFECT
THRESHOLD
METALS (mg/kg)
Antimony 1,900/200
Arsenic 32.000/3,200
Cadmium 1.100/580
Copper 49.00/9.700
BIOLOGICAL STATIONS
AND CONCENTRATIONS
EXCEEDING THRESHOLD
(mg/kg)
RS-22
RS-24
RS-18
RS-19
SI-11
RS-22
RS-20
RS-24
RS-18
RS-19
RS-22
RS-20
RS-24
RS-18
RS-19
SI-12
SI-11
RS-22
RS-24
RS-20
RS-18
RS-19
1,900
3,000
4,800
6,200
4,400
30,000
32,000
88.000
110.000
270,000
780
1.100
1,200
2,100
2.800
12,000
14.000
31 ,000
48.000
49,000
130,000
390,000
APPARENT BIOLOGICAL STATIONS
EFFECT AND CONCENTRATIONS
THRESHOLD EXCEEDING THRESHOLD
METALS (mg/kg) (mg/kg)
Lead 35.000/14.000 SI-11
SI-12
RS-22
RS-20
RS-24
RS-18
RS-19
Mercury 210/77 RS-20
~ RS-19
RS-18
Nickel 6.800b/6>300 RS-20
Zinc 72.000/12.000 SI-12
SI-11
RS-18
RS-20
RS-22
RS-19
RS-24
31,000
32,000
35.000
28.000
66,000
71.000
180.000
210
550
590
6.800
22.000
23,000
38,000
50.000
72 ,000
160.000
200,000
a Where two values are shown, the one on left Is the toxlclty threshold and the one on right Is the benthlc effects threshold.
The lower of these paired values Is underlined. Where only one value Is shown, the two apparent thresholds are Identical.
b No apparent toxlclty threshold was observed for this chemical. The value shown 1s the maximum concentration observed.
-------
TABLE 4.6. APPARENT EFFECT THRESHOLDS FOR POTENTIAL PROBLEM
ORGANIC COMPOUNDS NORMALIZED TO ORGANIC CARBON
ORGANIC COMPOUNDS
Phenol
2-Methylphenol
4-Methylphenol
LMU aromatic hydrocarbons
HHU aromatic hydrocarbons
Chlorinated benzenes
Chlorinated butadienes
Hexachlorobutadlene
Total phthalates
Total PCBs
Benzyl alcohol
Olbenzofuran
APPARENT
EFFECT
THRESHOLD
(ug/kg)
39,000b>c
5.300/10.000C
37.000/81.000
370.000/530.000|:
960.000/1. 500. 000C
20.000/<21 ,000<:
1.600,000
9.600/11.000
310.000b/290.0QO
Z5. 000/46 .000C
5.000
15.000/58.0QOC
BIOLOGICAL STATIONS
AND CONCENTRATIONS
EXCEEDING THRESHOLD
(ug/kg)
NONE
RS-13
SP-16
RS-13
SP-15
SP-14
RS-13
RS-13
RS-13
HY-«7
HY-42
HY-47
HY-22
RS-19
RS-20
HY-23
HY-22
HY-42
SP-16
RS-19
RS-18
RS-13
10,000
61 ,000
81 .000
1,300.000
590,000
530,000
1,500,000
21.000
2,500,000
11,000
16,000
16,000
300.000
310,000
40.000
45,000
46,000
8,800
19,000
23,000
58,000
ORGANIC COMPOUNDS
Aniline
N-Nltrosodlphenylamlne
Tetrach 1 oroethene
Ethylbenzene
Total xylenes
1-Methy l-2-( 1-methyl-
ethyljbenzene*
2-Methoxyphenol*
l.l'-Blphenyl*
Dlbenzothlophene*
Dlterpenold hydrocarbons
Isoplmaradlene'
Unidentified .
dlterpene8'1
Retene*
APPARENT
EFFECT
THRESHOLD
(ug/kg)
U 7.700d
ll,OOOb(C
22,000b'e
3.800b'c
12.000b>c
UO.OOQP/35.000
23,000
7.000/12.000*
8.200/14.000
74,000b'c
71.000/69.000
57.000/81.000
BIOLOGICAL STATIONS
AND CONCENTRATIONS
EXCEEDING THRESHOLD
(ug/kg)
CI-11
NONE
NONE
NONE
NONE
SI-11
SP-15
HY-17
SP-14
SP-14
SP-15
SP-16
RS-13
RS-18
RS-18
RS-13
RS-19
NONE
HY-47
SI-12
SI-11
RS-13
SI-15
SP-16
16,000
110,000
68.000
54,000
41.000
24.000
73.000
23.000
12.000
12,000
12,000
14,000
17.000
87,000
130,000
71,000
65,000
81,000
120,000
• Where two values are shown, the one on left Is the toxlclty threshold and the one on right Is the benthlc effects threshold. The lower of these
paired values Is underlined. Where only one value Is shown, the two apparent thresholds are Identical.
b No apparent toxlclty threshold was observed for this chemical. The value shown Is the Maximum concentration observed.
c No apparent benthlc effects threshold was observed for this chemical. The value shown Is the maximum concentration observed.
d Aniline was undetected at values ranging up to 7,700 ugAg OC at all stations except CI-11.
' This compound was Identified by matching the saiple spectra with library reference spectra. The Identification Is considered tentative because
standards of this compound are not routinely analyzed.
f Possibly kaur-16-ene.
-------
TABLE 4.7. SUMMARY OF EFFECTS AND POTENTIAL PROBLEM CHEMICALS AT
BIOLOGICAL STATIONS (NORMALIZED TO ORGANIC CARBON)
Toxicity
and /or
Benthic Effect^
0
M
0 M C
0 A M C
0AM P T
M C T
M
A
0 M
A
A
C
A C
A
A
A
0
0 A M C P T
0 A M C
0 A T
0AM
0 M C P T
0 M C P T
0 A
0 A
0 A M C P T
0AM
M
Ae
Station
HY-12
HY-14
HY-17
HY-22
HY-23
HY-32
HY-37
HY-42
HY-47
B-15
BL-25
SI-11
SI-12
SI-15
MI-11
MI-15
SP-12
SP-14
SP-15
SP-16
CI-11
CI-13
CI-16
CI-20
RS-13
RS-18
RS-19
RS-20
RS-24
Chemical0 Exceeding An Apparent Effect Threshold
HCBD, TPCBb
TPCB
HCBD, TPCBC
HCBD, CBEN
ASd, Cud, Pbd, Znd
Cud, Pbd, Znd
RETC
4MNOL, MOX
4MNOL, MOX
4MNOLC, BZOH, MOX, RET
ANIL
2MNOLC, LPAHC, HPAHC, CBEN, DBFC, BIPHC, DIBC, RETC
DBFC BIPHC, DIBC, sbj As f cd , Cu , Pb, Hg , Znd
PHTHQ, DBFC, DIB> Sbj AS cd , Cu, Pb, Hg, Zn
PHTHd, Asd, Cdd, Cud, Pbd, Hgd, Nid, Znd
Sb, As, Cd, Cu, Pb, Zn
NOTE: See Table 4.4 for footnotes.
4.16
-------
TABLE 4.8. APPARENT EFFECT THRESHOLDS FOR POTENTIAL PROBLEM
CHEMICALS NORMALIZED TO FINE-GRAINED MATERIAL
METALS
Antimony
Arsenic
Cadmium
Copper
APPARENT
EFFECT BIOLOGICAL STATIONS AND
THRESHOLD CONCENTRATIONS EXCEEDING
(mg/kg) THRESHOLD (mg/kg) METALS
410/11 RS-20
~ RS-24
RS-22
RS-19
RS-18
6,600/160 RS-20
RS-24
RS-22
RS-18
RS-19
170/25 RS-20
~ RS-24
RS-22
RS-19
RS-18
6,800/550 RS-24
RS-20
RS-22
RS-18
RS-19
31 Lead
160
410
1100
1300
1,500
4.400
6,600 Mercury
29.000
48,000
52 Nickel
60
170
500
550
Z1nc
2,400
2.400
6.800
34,000
70,000
APPARENT
EFFECT BIOLOGICAL STATIONS AND
THRESHOLD CONCENTRATIONS EXCEEDING
(mg/kg) THRESHOLD (mg/kg)
7,700/790 SI-11
RS-20
RS-22
RS-24
RS-18
RS-19
CI-11
11/3.6 RS-20
RS-22
RS-19
RS-18
780b/250 RS-18
RS-20
RS-19
RS-22
16.000/640 CI-11
RS-20
RS-18
RS-24
RS-22
RS-19
830
1,300
7,700
3,300
19.000
32.000
1.800
10
11
100
160
280
330
720
780
830
2.400
10.000
10.000
16,000
28,000
a Where two values are shown, the one on left 1s the toxldty threshold and the one on right Is the benthlc effects threshold. The lower of these
paired values Is underlined. Where only one value Is shown, the two apparent thresholds are Identical.
b No apparent toxldty threshold was observed for this chemical. The vlaue shown 1s the maximum concentration observed.
-------
TABLE 4.9. APPARENT EFFECT THRESHOLDS FOR POTENTIAL PROBLEM
ORGANIC COMPOUNDS NORMALIZED TO FINE-GRAINED MATERIAL
ORGANIC COMPOUNDS
Phenol
2-Methylphenol
4-Methylphenol
LMU aronatlc hydrocarbons
HMU arcMtlc hydrocarbons
Chlorinated benzenes
Chlorinated butadienes
Hexachlorobutadlene
Total phthalates
Total PCBs
lenzyl alcohol
Dlbenzofuran
Aniline
APPARENT
EFFECT
THRESHOLD
(ug/kg)
3.800b/l .800
780b/570
1.200/4.500
16.000/29.000
42.000/82.000
2.300b/1.200
82,000b>c
2,000b/580
21.000
1,200/1.400
780b/180
•^_~
960/3.200
1)1600"
IIOL06ICAL STATIONS
AND CONCENTRATIONS
EXCEEDING THRESHOLD
(ug/kg)
SP-14
CI-11
RS-19
RS-22
RS-22
SP-16
CI-16
RS-13
SP-1S
SP-14
RS-13
RS-19
RS-1B
RS-13
RS-18
RS-19
HY-22
RS-22
NONE
HY-22
RS-22
RS-19
HY-42
HY-23
HY-22
SP-14
RS-19
RS-22
RS-13
RS-19
RS-18
CI-11
2,600
2.800
3.100
3,800
780
1.600
1,600
4,500
10.000
140,000
29.000
40,000
61,000
82,000
93,000
98.000
1.800
2.300
970
2,000
54,000
1.400
1.700
2.600
240
310
780
3.200
3.400
6,000
3.600
APPARENT
EFFECT
THRESHOLD
ORGANIC COMPOUNDS (ug/kg)
N-N1trosod1phenylaBlne 500
h r
Tetrachloroethene 1,000 •
(or other volatile*)
l-Methy1-2-(l-«ethyl-
•thyl)benzenee 2.900/2.000
2-Methoxyphenole 1.700
l.l'-Blphenyie 460/640
2-Hethy1phenanthrenee 930/1.400
l-Methy1pyrene« 500/600
Dlbenzothlophene8 430/780
K f
Pentachlorocyclopentane* 130D'e
Dlterpenold hydrocarbons
Isop1marad1enee 2.700
Unidentified . 3,500
d1terpene*'T
Retene* 2.300/3.600C
BIOLOGICAL STATIONS
AND CONCENTRATIONS
EXCEEDING THRESHOLD
(ug/kg)
RS-18
NONE
si-n
HY-17
SP-15
SP-14
SP-15
SP-14
SP-14
RS-13
RS-19
RS-18
HY-22
RS-13
RS-19
RS-18
RS-13
HY-22
HY-17
RS-18
RS-19
CI-11
RS-19
RS-18
NONE
SP-14
SP-15
SP-14
RS-19
SP-16
RS-13
1.800
2,900
4,200
5,400
9.900
5,800
5,900
470
640
720
3.300
980
1,400
3,100
7,200
800
1,600
2,200
2,600
2.800
480
3,000
3,300
8,900
4,200
7,800
3.000
3.100
3.600
• Where two values are shown, the one on left 1s the toxldty threshold and the one on right Is the benthlc effects threshold. The lower of these
paired values 1s underlined. Where only one value Is shown, the two apparent thresholds are Identical.
b No apparent toxlclty threshold was observed for this chealcal. The value shown Is the nxtwrn concentration observed.
c No apparent benthlc effects threshold was observed for this chenlcal. The value shown Is the MaxlMum concentration observed.
d Aniline was undetected at concentrations ranging up to 360 ug/kg fine grained Material at all stations except CI-11.
« This compound was Identified by Hatching the sample spectra with library reference spectra. The Identification 1s considered tentative because
standards of this compound are not routinely analyzed.
' Possibly kaur-16-ene.
4.18
-------
TABLE 4.10. SUMMARY OF EFFECTS AND POTENTIAL PROBLEM CHEMICALS AT BIOLOGICAL
STATIONS (NORMALIZED TO FINE-GRAINED MATERIAL)
Toxic ity
and/or
Effects
0
M
0 M C
0 A M C
0AM P T
M C T
M
A
0 M
A
A
C
A C
A
A
A
0
0 A M C P T
0 A M C
0 A T
0AM
0 M C P T
0 M C P T
0 A
0 A
0 A M C P T
0AM
M
Ae
Station
HY-12
HY-14
HY-17
HY-22
HY-23
HY-32
HY-37
HY-42
HY-47
B-15
BL-25
SI-11
SI-12
SI-15
MI-11
MI-15
SP-12
SP-14
SP-15
SP-16
CI-11
CI-13
CI-16
CI-20
RS-13
RS-18
RS-19
RS-20
RS-24
Chemical*3 Exceeding An Apparent Effect Threshold
MBEN, MPYR
CBENd, HCBDd, TPCB, MPHENC, MPYR
TPCB
TPCBC
MBENd, Pbd
PNOLd, 4MNOL, BZOHd, MBEN, MOX, BIPH^, DTP
4MNOL) MBEN, MOX
4MNOLC, RETC
PNOLd, DIBC, Pbd, Znd
4MNOLC
LPAHC, MPYRC, HPAHC, 4MNOLC, DBFC, BIPHC, MPHENC, RETC
LPAH, HPAH, NDPA, DBF, BIPH, DIB, MPHEN, MPYR, Sb, As, Cd
Cu, Pb, Hg, Znd
LPAH, HPAH, PHTH, PNOLd, DBF, BZOHd, BIPH, DIB, MPHEN, RETC
MPYR, Sb, As, Cd, Cu, Pb, Hg, Nid, Zn
Sbd, Asd, Cd<3, Pbd, Hgd, Nid, Znd
SBd, Asd, Cdd, Cud, Pbd, Znd
NOTE: See Table 4.4 for footnotes.
4.19
-------
The rationale for evaluating potential contaminant relationships with sediment
toxicity and biological effects based on these normalizations was summarized
in Section 3.1.2. Briefly, effects may be produced by contaminants found
in low concentration when normalized to dry weight but present in high
concentration when normalized to organic carbon or fine-grained sediments
(two major chemical binding factors in sediments).
The purpose of Tables 4.5-4.10 is to compare the distribution of potential
problem chemicals with that indicated in Table 4.4 for dry-weight normalized
concentrations. Chemicals exceeding an AET at selected stations regardless
of the method of normalization included:
• Chlorinated compounds, including total PCBs and hexachlorobutadiene
• Low and high molecular weight PAH
• 4-Methylphenol
• Bis-2-(ethylhexyl)phthalate and di-n-butylphthalate esters
• All metals of concern, including antimony, arsenic, cadmium,
copper, lead, mercury, nickel, and zinc.
Organic carbon and percent fine-grained material normalizations did
not reveal any chemicals above either their toxicity or benthic AET at
the six stations (20 percent) discussed previously where AET were not exceeded
on a dry-weight basis. Chemicals were below both AET at 48 percent (14/29)
of the "affected" stations when normalized to total organic carbon. Chemicals
were below both AET at the same percentage of stations (different distribution)
when normalized to percent fine-grained material. For most sediments with
multiple toxicity and benthic effects, chemicals exceeded an AET regardless
of normalization. An obvious exception was City Waterway, where none of
the sediments, including three samples with multiple significant bioassay
and benthic responses, had chemicals exceeding the toxicity or benthic
effects AET when normalized to organic carbon. These three stations had
high concentrations of both chemicals (DW) and organic carbon. These data
suggest either that high concentrations (DW) of chemicals were associated
with effects regardless of organic carbon-normalized concentrations, or
that observed effects resulted solely from organic enrichment. The relation-
ships among these factors for City Waterway are discussed in the following
section.
Some chemicals listed in Tables 4.7 and 4.10 were present at low
concentration (DW), but were found at relatively high levels with respect
to the organic carbon content or percent fine-grained material of the
sediments. For example, at Station RS-13, 2-methylphenol was the only
chemical elevated above the sediment toxicity threshold when normalized
to dry-weight (Table 4.4). After normalization to organic carbon or percent
fine-grained material, concentrations of eight chemicals or chemical groups
exceeded an AET at Station RS-13. For the purpose of identifying potential
problem chemicals, all chemicals shown in Tables 4.4, 4.7, and 4.10 were
evaluated further. In the following section, a correspondence between
site-specific gradients of chemical concentrations and toxicity or benthic
effects is shown for several of these chemicals.
4.20
-------
Chemicals of concern defined in Section 3.1 that never exceeded an AET
(regardless of concentration normalization) are summarized in Table 4.11.
These chemicals were not considered to have a high priority for further
evaluation of their potential relationship to sediment toxicity or benthic
effects, even when found at high elevations above Puget Sound reference
conditions.
4.2.3 Correspondence Among Chemical, Toxicity and Benthic Effects Gradients
Gradients in toxicity and benthic effects were observed along four
transects in Commencement Bay study areas. These included a cross-channel
transect of stations in Hylebos Segment 2 (HY-22, HY-23, HY-24), a transect
of stations in St. Paul Waterway (SP-14, SP-15, SP-16, SP-12, SP-11) , a
transect at the head of City Waterway in Segment 1 (CI-11, CI-13, CI-17),
and a transect running offshore along the Ruston-Pt. Defiance Shoreline
in Segment 2 (RS-18, RS-19, RS-20). Stations located on these transects
included 11 of the 29 stations with significant sediment toxicity or benthic
effects and all of the stations with the most extreme effects (e.g., sediment
toxicity exceeding 50 percent mortality and abnormality plus multiple
depressions of the five benthic indicators).
In this section, concentration gradients of chemicals exceeding an
AET are correlated with toxicity and benthic effects gradients along each
transect. The discussion focuses on chemicals with concentrations exceeding
apparent effect thresholds regardless of the normalization used. The
substantial change in DW concentrations of these chemicals along the four
transects resulted in clear trends for potential problem chemicals in each
area. Linear correlation analysis and factor analysis (varimax rotation)
of data subsets were used to corroborate possible relationships among the
chemical, toxicity, and benthic effects variables that are summarized in
the summary plots within these sections.
4.2.3.1 Hylebos Waterway--
Within Hylebos Waterway, multiple significant bioassay responses and
benthic effects were observed only at Stations HY-22 and HY-23 in Segment 2.
Toxicity and benthic effects generally decreased cross-channel from Station
HY-22 to Station HY-24 (e.g., see Figures 3.44 and 3.49 in Section 3.3).
Total PCBs and hexachlorobutadiene exceeded apparent effect thresholds
for either sediment toxicity or benthic effects regardless of normalization
at Station HY-22 (Tables 4.4, 4.7, and 4.10). The correspondence among
total PCB concentrations, amphipod mortality, and oyster larvae abnormality
is shown in Figure 4.3 for these stations.
Stations HY-42, HY-43, and HY-44 constituted a second cross-channel
transect in Hylebos Segment 5. Total PCBs were also elevated above the
AET at Station HY-42 regardless of the means of normalization. Total PCB
data for these latter three stations are also included for comparison in
Figure 4.3. Amphipod mortality and oyster larvae abnormality decreased
with decreasing PCB concentrations (DW) along both transects.
4.21
-------
TABLE 4.11. CHEMICALS OF CONCERN WITH CONCENTRATIONS
NEVER EXCEEDING APPARENT EFFECT THRESHOLDS
Chemical of Concern^ Concentration Range With No Effects Observed
(ug/kg dry-weight)
Beryllium 80 - 450
Chromium 5,400 - 37,000
Silver 80 - 560
1 ,3-Dichlorobenzene
Butylbenzyl phthalate
Di-n-octyl phthalate
Diethyl phthalate
Trichlorinated butadienes
Tetrachlorinated butadienes
Ut>
U
U
1
14
6
2
5
10
170
470
420
73
- 30,000
- 14,000
a Chemicals of concern are those present in at least some Commencement
Bay sediments at concentrations that exceed all Puget Sound reference
conditions.
b U: Undetected at the detection limit indicated for the lower range
of concentrations.
4.22
-------
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-------
Although concentrations of other chemicals exceeded the toxicity AET
along both transects, only PCBs showed strong linear relationships along
both transects. For example, although hexachlorobutadiene (HCBD) concentrations
exceeded the toxicity AET at Stations HY-22 and HY-23 in Segment 2, and
at Station HY-42 in Segment 5, and corresponded generally to observed toxicity,
the relationships within each transect differed.
Linear trends did not emerge for several other contaminants with concentra-
tions (DW) exceeding an AET at Station HY-22. For example, although phenol
concentrations exceeded the threshold, a linear exposure-response relationship
was not observed (Figure 4.3).
Mollusca was the only taxon significantly depressed at stations over
the entire length of Hylebos Waterway. Total mollusc abundance consistently
decreased with increasing total PCB concentrations at Stations HY-24, HY-23,
and HY-22 (e.g., Figure 4.4). Total infauna and polychaete abundances
were significantly depressed only at Station HY-23 along this transect,
although the overall chemical contamination at Station HY-22 was higher.
These latter variables showed no linear relationship with PCB concentrations.
The abundances of total taxa and polychaetes decreased with increasing
nickel concentrations (DW) along the transect as shown in Figure 4.4.
The linear correlation of these relationships improved after normalization
to organic carbon, but nickel exceeded its AET at Station HY-22 and HY-23
only when normalized to dry-weight. Changes in arsenic or other metal
concentrations (DW) did not correspond with observed benthic effects gradients.
Within Hylebos Waterway, stronger relationships were found between
contaminants and sediment toxicity than between contaminants and benthic
effects. Organic compounds, especially PCBs, dominated the list of potential
problem chemicals in the waterway. Although metals contamination in upper
Hylebos Waterway was significant, toxicity or benthic effects gradients
did not appear to correspond with concentration gradients of metals, with
the possible exception of nickel.
4.2.3.2 St. Paul Waterway —
Within St. Paul Waterway, 100 percent mortality and abnormality and
significant depressions of all major taxa groups were found at Station
SP-14 off the main outfall of Champion International. Organic enrichment
resulting in sediment anoxia may have contributed to the observed effects,
at least at SP-14 (see Figure 3.3). Station SP-15, located on a transect
away from the main outfall also had high mortality and abnormality (>50 percent)
and exhibited significant depressions of Mollusca and Crustacea. Organic
enrichment (only 2.1 percent TOC) did not appear to be a factor at this
station. TOC, total volatile solids (4.3 percent) and sulfide content
(minimum estimate of 2.6 mg/kg DW) resembled those found in sediments from
nonurbanized regions of Puget Sound. Therefore, given the gross physicochemical
differences observed at SP-14 and SP-15, the observed high level of toxicity
and benthic effects at both these stations did not appear to be related
solely to conventional factors (e.g., organic enrichment).
4-Methylphenol was found at elevated concentrations (DW) that decreased
with distance from Station SP-14 off the main outfall. The linear relationship
of sediment toxicity to 4-methylphenol concentration at the five stations
4.24
-------
4h
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POLYCHAETE ABUNDANCE TOTAL ABUNDANCE MOLLUSC ABUNDANCE
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in St. Paul Waterway (Figure 4.5) suggested that the toxicity gradient
resulted from 4-methylphenol or from a contaminant with a spatial distribution
similar to that of 4-methylphenol. Extrapolation of this strong trend
[excluding the high concentration (and 100 percent mortalitiy and abnormality)
found at Station SP-14] suggest that 100 percent mortality and abnormality
might be expected at 4-methylphenol concentrations exceeding 4,000 and
4,800 ug/kg DW, respectively.
2-Methoxyphenol and phenol were also elevated above an AET regardless
of concentration normalization along this transect, but did not show the
consistent gradient with sediment toxicity as found for 4-methylphenol
(Figure 4.5). Retene concentrations, which peaked at Station SP-16, correlated
negatively with the toxicity and benthic effects gradients.
Benthic effects in St. Paul Waterway, were not correlated as well
with individual contaminant concentrations as were sediment toxicity
indicators. All four major benthic taxa were significantly depressed at
Station SP-14. Total crustacean abundances consistently increased with
decreasing 4-methylphenol concentrations (Figure 4.6), although mollusc
abundances did not. Mollusc abundances were best correlated with the
distribution of the tentatively identified l-methyl-2-(l-methylethyl)benzene
(Figure 4.6). Total taxa and polychaete abundances showed no consistent
trend with any contaminant concentration along the transect, although both
indicators were significantly depressed at Station SP-14, where highest
concentrations of several of the contaminants were found. There were no
strong correlations between indicators of sediment toxicity or benthic
effects and indicators of organic enrichment (i.e., TOC, TVS).
Organic compound contamination apparently was a major factor associated
with significant toxicity and benthic effects in St. Paul Waterway. Except
for nickel (at Station SP-14 only), no metals exceeded either AET in the
waterway, and nickel did not correlate with observed effects. 4-Methylphenol
was the only contaminant having a concentration trend consistent with the
toxicity trend along the entire waterway. Concentrations of this alkylated
phenol also showed some relationship with the observed change in crustacean
abundances. Two tentatively identified organic compounds had stronger
correlations with the depressions observed for molluscs. Total taxa and
polychaetes also may have been affected by these contaminants, but a clear
relationship was not apparent.
4.2.3.3 City Waterway--
Multiple sediment toxicity and benthic effects were observed in City
Waterway. Effects decreased with distance from the head of the waterway
(Stations CI-11, CI-13, and CI-17). Severe effects were also observed
at the single biological station in the Wheeler-Osgood branch of the waterway,
but sediments in this isolated arm of City Waterway appeared to be chemically
distinct from those in the main portion of the waterway and are not included
in the following discussion.
Unlike the areas already discussed, there were no chemical contaminants
that exceeded either AET in City Waterway when normalized to percent TOC,
even at the most severely affected stations. The decline in sediment toxicity
away from the head of City Waterway was accompanied by a decline in TOC,
4.26
-------
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as shown in Figure 4.7. A similar decline was observed for lead and zinc
concentrations (DW). The observed toxicity correlated more closely with
TOC than with any other contaminant. There are insufficient data to determine
whether the observed toxicity resulted from toxic contaminants or organic
enrichment, although TOC levels were nearly twice as high at some stations
in other waterways without significant toxicity or benthic effects. At
the head of City Waterway, the source of organic enrichment appeared to
be the source of toxicity, as well as the cause of depressed abundances
of molluscs and Crustacea (e.g., Figure 4.8). An exception to these trends
was observed for polychaete abundances, which were most depressed at Station
CI-13. Polychaete abundances decreased in direct proportion to increasing
mercury concentrations, as shown in Figure 4.8.
4.2.3.4 Ruston-Pt. Defiance Shoreline--
High levels of all metals and several organic compounds were observed
at Station RS-18, located directly off the main outfall of ASARCO along
the Ruston-Pt. Defiance Shoreline. Concentrations of all of these contaminants
generally decreased along an onshore-offshore transect of biological stations
including RS-18, RS-19, and RS-20. This decrease in contamination corresponded
to a decrease in sediment toxicity and benthic effects along the transect.
The strongest linear correlations between contaminant concentrations and
sediment toxicity were found for mercury and low molecular weight PAH (LPAH),
which had identical distributions along this transect. Plots for concentrations
of mercury normalized to DW and percent fine-grained material are shown
in Figure 4.9. LPAH showed a similar trend with sediment toxicity regardless
of the method of normalization. A decrease in sediment toxicity along
the transect also corresponded with a general decrease of arsenic concentrations
normalized to DW (Figure 4.9). However, following normalization to organic
carbon or percent fine-grained material, the linear trend was disrupted.
The distribution for arsenic was typical of that observed for most other
contaminants (i.e., a general linear trend only when concentrations were
normal i zed to DW).
Mollusc and polychaete abundances decreased to zero with increasing
concentrations of most contaminants along the RS-20, RS-19, RS-18 transect
(Figure 4.10). The major difference in the relationships was that mollusc
abundances appeared to decrease exponentially while polychaete abundances
decreased linearly with concentrations (DW) of various metals and organic
compounds. Total crustacean and total taxa abundances were higher at RS-19
than at RS-20, which did not correspond with the concentration gradients
of any contaminant normalized to dry weight.
4.2.4 Summary
A general correspondence of higher sediment contaminant concentrations,
higher sediment toxicity, and lower benthic infaunal abundances was observed
throughout the study area. Toxicity or benthic AET (i.e., the concentration
above which all sediments had significant toxicity or benthic effects,
respectively) were exceeded by a number of chemicals at most, but not all,
of the 29 biological stations exhibiting significant effects. The six
stations that did not have any chemicals above their toxicity or benthic
AET (DW) were unusual in that the effects recorded by one biological indicator
were not reflected by significant responses by the other biological indicators.
4.29
-------
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Figure 4.8. Correlation plots of benthic indicators and
selected chemicals at the head of City Water-
way (Stations CI-11, CI-13, and CI-17).
4.31
-------
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Most of these stations exhibited toxicity by the amphipod bioassay only,
and the toxicity may have been related to the high percentage of fine-grained
material (>80 percent) at each station. A difference in the toxicity and
benthic effects threshold for several chemicals suggests that the bioassays
were more sensitive to organic compound contamination and benthic depressions
were more sensitive to metals contamination.
An analysis of effects gradients was possible along four transects
of biological stations in Commencement Bay. Strong relationships were
observed for a limited number of the chemicals that exceeded an AET in
each of these areas. Patterns consistent with exposure-response relationships
included:
• PCB concentrations, sediment toxicity, and mollusc abundance
along a Hylebos Waterway transect
• 4-Methylphenol concentrations, sediment toxicity, and crustacean
abundance along a St. Paul Waterway transect
• Organic enrichment, lead, zinc, sediment toxicity, mollusc
abundance, and crustacean abundance along a City Waterway
transect
t Mercury concentrations and polychaete abundance along the
same City Waterway transect
• Mercury and LPAH concentrations, and sediment toxicity along
a Ruston-Pt. Defiance transect leading offshore
• Most metal and organic compound concentrations with mollusc
and polychaete abundances along the same Ruston-Pt. Defiance
Shoreline transect.
The stations along these four transects included those stations with
the most extensive toxicity and benthic effects observed in Commencement
Bay. Sediment toxicity tended to correlate better with contaminant concentra-
tions than did benthic effects. Because bioassays were conducted on an
aliquot of the same homogenized sediment sample used for chemical analyses,
whereas benthic samples were collected synoptically with the bioassay-chemistry
samples, but were not the identical sediments, some of the variability
associated with contaminant-benthic infauna relationships may reflect random
variability at the site.
4.3 COMPARISON OF BIOASSAY RESPONSES WITH BENTHIC INVERTEBRATE ASSEMBLAGES
This section examines the degree of consistency between bioassays
and benthic infauna as indicators of environmental contamination. In the
present study, each indicator was used to determine a different type of
response. Bioassays represented the acute (i.e., hours to days) responses
of individual species (i.e., Rhepoxinius abronius, Crassostrea gigas) to
sediment removed from its natural setting, whereas benthic infauna represented
the in situ chronic (i.e., weeks to months) responses of groups of organisms
(i.e., major taxa). The primary objective of the following comparisons
is to determine whether the two indicators gave similar patterns with respect
4.34
-------
to identifying contaminated areas. If the patterns are similar, future
studies may be able to rely on only one of these indicators. Comparisons
were based on the 48 stations at which both indicators were evaluated in
March, 1984.
4.3.1 Correlation of Indicators
Amphipod mortality and oyster abnormality were correlated with the
abundances of five major benthic invertebrate taxa (total taxa, Polychaeta,
Mollusca, Crustacea, and Echinodermata) using the product-moment correlation
coefficient (Table 4.12). All but one of the correlation coefficients
(total taxa-oyster abnormality) was negative. However, none of the coefficients
was significant (P>0.05). These results indicate that simple linear relation-
ships did not exist between bioassay responses and the abundances of major
benthic invertebrate taxa.
4.3.2 Comparison of Bioassays with Benthic Groupings
Values of amphipod mortality and oyster abnormality were compared
with the groupings of stations determined by classification analysis of
benthic invertebrate assemblages (Section 3.2). This comparison was made
to determine whether stations with different benthic assemblages (based on
species composition and abundance) exhibited different (or characteristic)
bioassay responses.
Results were similar for both the amphipod and oyster bioassays (Figure
4.11). Bioassay values for Groups I-VII overlapped considerably, indicating
that characteristic bioassay responses did not correspond to these different
benthic assemblages. All bioassay values for Groups I-VII were less than
50 percent.
Bioassay values for Group VIII and the three ungrouped (i.e., unique)
stations (RS-18, RS-19, and SP-14) did not overlap with values from Groups
I-VII and, except for oyster abnormality at RS-19 (47 percent), exceeded
50 percent. Benthic assemblages at all of these stations were considerably
different from those found at the remaining stations sampled in this study.
Group VIII consisted of Stations CI-11 and SP-15, where nematodes and Capitel la
capitata dominated benthic assemblages. Also, abundances of molluscs at
CI-11 and SP-15 (4 and 50 individuals/m2, respectively) were third and
fifth lowest in the study. Stations RS-18 and SP-14 had the lowest abundances
of total benthic invertebrates (29 and 133 individuals/m2, respectively)
in the study. In addition, polychaetes and molluscs were absent from Station
RS-18 and molluscs were absent from Station SP-14. These were the only
stations at which these major taxa were absent. Finally, Station RS-19
had the fourth lowest abundance of molluscs (33 individuals/m2) in the
study. Thus, bioassay values greater than 50 percent identified tne most
unique (and presumably most severely impacted) benthic assemblages in the
study.
4.3.3 Comparison of Significant Responses
The relationship of significant and nonsignificant amphipod and oyster
larvae bioassay results (Section 3.3) to presence or absence of one or
more significantly depressed benthic invertebrate taxa (Section 3.2) at
4.35
-------
TABLE 4.12. CORRELATIONS'* OF ABUNDANCES OF MAJOR BENTHIC INVERTEBRATE
TAXA WITH AMPHIPOD MORTALITY AND OYSTER LARVAE ABNORMALITY
Taxon
Total taxa
Polychaeta
Mollusca
Crustacea
Echinodermata
Amphipod
-0.
-0.
-0.
-0.
-0.
Mortality
04
23
24
10
21
nsb
ns
ns
ns
ns
Oyster
0
-0
-0
-0
-0
Abnormal
.00
.22
.33
.22
.22
ns
ns
ns
ns
ns
ity
a The product-moment correlation coefficient was calculated for the 48
stations at which benthic infauna and bioassays were both evaluated in
March, 1984.
b ns = not significant at an experimentwise error rate of 0.05. Critical
correlation coefficient = 0.37.
4.36
-------
100 H
75 -
OJ
UJ
0.
25 -
AMPHIPOD MORTALITY
I
SP-14
RS-18
RS-19
CI-11
+
SP-15
.I'll
uu
o
CC
UJ
QL
100 -i
75 -
50 -
25-
SP-14 •
OYSTER ABNORMALITY
CI-11
+
SP-15
RS-18 '
RS-19 •
I'-l'.l
IV V VI VII VIII UNGROUPED
STATION GROUPS
Figure 4.11.
Ranges of bioassay responses for the station
groupings based on classification analysis of
benthic assemblages.
4.37
-------
the 48 study sites sampled in March is presented in Figure 4.12. The
distributions of responses for both bioassays were very similar. Amphipod
mortality was consistent with benthic depressions at 66.6 percent (32/48)
of the stations, whereas oyster abnormality was consistent at 79.2 percent
(38/44) of the stations. Amphipod mortality and oyster abnormality did
not confirm the presence of one or more benthic depressions at 18.8 percent
(9/48) and 12.5 percent (6/48) of the stations, respectively. Conversely,
amphipod mortality and oyster abnormality did not confirm the absence of
benthic depressions at 14.6 percent (7/48) and 8.3 percent (4/48) of the
stations, respectively.
Results of these comparisons suggest that the amphipod and oyster
bioassays are similarly accurate in confirming impacts on benthic inverte-
brates. However, this accuracy is less than 70 percent for the amphipod
bioassay and less than 80 percent for the oyster bioassay.
4.3.4 Summary
Simple linear relationships were not found between abundances of major
benthic invertebrate taxa and either amphipod mortality or oyster larvae
abnormality. Bioassay values less than 50 percent were not able to distinguish
or characterize different benthic assemblages. Bioassay values greater
than 50 percent accurately identified the most unique (and probably most
severely impacted) benthic assemblages in the study. Significant amphipod
mortalities and oyster abnormalities corresponded with the presence of
one or more significant depressions of major benthic invertebrate taxa
at 66.6 and 79.2 percent (respectively) of the stations sampled.
4.4 COMPARISONS OF LESION PREVALENCES IN ENGLISH SOLE WITH CHEMICAL CONTAMI-
NANTS IN SEDIMENTS
Mai ins et al . (1984) found that prevalences of total hepatic lesions
in English sole from 32 stations in Puget Sound were positively correlated
(P<0.05, Spearman rs) with sediment concentrations of PAH and metals.
To test whether similar relationships existed in the present study, prevalences
of English sole with one or more of the four hepatic lesions (Section 3.5)
were compared with sediment concentrations of major classes of chemical
contaminants at stations near the trawl transects. Chemical groups included
PAH, metals (except iron and manganese) , PCBs, chlorinated benzenes, and
phthalates. Comparisons were based on 16 stations (Carr Inlet plus the
15 trawl transects in Commencement Bay) and were made using the Spearman
rank correlation coefficient. Each correlation was tested at a comparisonwise
error rate of 0.01 so that the experimentwise rate was 0.05. The critical
rs value for each comparison was 0.62.
Although all five correlations were positive (Figures 4.13 and 4.14),
none was significant (P>0.05). The highest correlations were found between
lesion prevalence and PAH (rs=0.55) and lesion prevalence and PCBs (rs=0.50).
Several factors limit comparisons between results of the present study
and those of Malins et al. (1984). Although lesion classifications were
standardized between studies, prevalences were based on different age
distributions of English sole. Because prevalences of at least two kinds
of lesions are functions of age (Section 3.5), between-study differences
4.38
-------
BIOASSAY
RESPONSE
BENTHOS AND BIOASSAY CONSISTENT
BENTHOS AND BIOASSAY INCONSISTENT
TOTAL NO. STATIONS EVALUATED = 48
AMPHIPOD MORTALITY
BENTHIC DEPRESSION
YES NO
YES
NO
OYSTER ABNORMALITY
BIOASSAY
RESPONSE
BENTHIC DEPRESSION
YES NO
YES
NO
Figure 4.12.
Correspondence between stations having signifi-
cant (P<0.05) bioassay responses and stations
having significant (P<0.05) benthic depressions.
4.39
-------
co
CO
111
_1
o
I
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X
ai
a:
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40 -l
30-
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40
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LU 30-
O
LU
LU „„ j
DC 20 1
Q.
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rs = 0.55 ns
• Cl 70
Cl 72
5 10 15 20 25
PAH CONCENTRATION (mg/kg DW)
rs = 0.19 ns
(1,894)
(3.206)
200 400 600 800
METALS CONCENTRATION (mg/kg DW)
l
1,000
Figure 4.13.
Correlations of lesion prevalence in English
sole with sediment concentrations of PAH and
metals, ns = P>0.05, experimentwise.
4.40
-------
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30 -
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•
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50 100 150 200 250 300 350
PCBs CONCENTRATION (pig/kg DW)
r. = 0.13 ns
50 100 150 200 250 300 350
g CHLORINATED BENZENES CONCENTRATION
J 0-g/kg DW)
>
30 -
20 -
10 -
rs = 0.16 ns
0 500 1,000 1,500 2,000 2,500 3,000 3,500
PHTHALATES CONCENTRATION (p0.05, experimentwise.
4.41
-------
in age distributions may have influenced correlation results. Also, the
suite of compounds used in the correlation analyses were not identical
between studies. Thus, between-study differences in correlation results
may have been due partly to differences in the chemical groups with which
lesion prevalences were compared.
Correlations between lesion prevalence and PAH and metals in the present
study were evaluated qualitatively to determine whether they showed any
similarities to the patterns found by Malins et al. (1984). As noted
previously, Malins et al. (1984) found significant correlations (P<0.05)
for these chemical groups, whereas the present study did not find significant
correlations (P>0.05).
The observed correlation with metals showed no similarities with the
results of Malins et al. (1984). The correlation coefficient in the present
study was 0.19, compared with the value of 0.54 found by Malins et al. (1984).
Furthermore, lesion prevalence at the two stations with the highest metals
concentrations (11.7 and 8.3 percent) were similar to the prevalence found
at the reference site (6.6 percent).
By contrast with metals concentrations, the observed correlation with
PAH concentration showed several similarities with the results of Malins
et al. (1984). The correlation coefficient in the present study (0.55)
was similar to the value found by Malins et al. (1984) (0.58). The reason
the former coefficient was not significant whereas the latter coefficient
was significant is due largely to differences in sample size between the
present study (n=17) and Malins et al. (1984) (n=32). As it stands, the
correlation coefficient in the present study (0.55) is very close to the
critical coefficient for significance (0.62). Furthermore, if the only
two apparent outliers to a monotonically increasing trend of lesion prevalence
with increasing PAH concentration (Stations CI-70 and CI-72) are removed
from the analysis, the correlation coefficient increases to 0.82, and becomes
highly significant (P<0.001, experimentwise). It is interesting that the
only two apparent outliers are both from City Waterway. This suggests
that patterns in this waterway are unique compared to those of the other
study areas. That is, although PAH concentrations at both trawl transects
in City Waterway were ranked second and third in magnitude in the entire
study, lesion prevalence was not exceptionally high (10.0 and 16.7 percent).
Although Malins et al . (1984) also found that PAH concentrations in City
Waterway (i.e., Station 23) ranked second in magnitude in their study,
they did not present the lesion prevalence specific to that station.
In summary, lesion prevalence in the present study did not correlate
significantly (P>0.05) with sediment concentrations of PAH, metals, PCBs,
chlorinated benzenes, and phthalates. If the pattern found for City Waterway
is considered unique and is removed from consideration, the correlation
between lesion prevalence and PAH concentration becomes highly significant.
4.5 RELATIONSHIP BETWEEN BIOACCUMULATION AND SEDIMENT CONTAMINATION
This section examines the relationships between sediment contamination
and bioaccumulation in English sole and crabs. The objectives are to identify
the sediment contaminants that are available for bioaccumulation in indigenous
4.42
-------
organisms and to determine sediment contaminant levels above which significant
bioaccumulation occurs.
4.5.1 Inorganic Substances
Sediments throughout the Commencement Bay waterways had varying elevations
of inorganic substances, with concentrations generally less than 25 times
reference values. Highest sediment concentrations of inorganic substances
occurred along the Ruston-Pt. Defiance Shoreline, where concentrations
of arsenic, copper, and lead were two to three orders of magnitude higher
than reference values. Despite these levels of sediment contamination,
fishes and crabs from Commencement Bay showed little evidence of tissue
accumulation of inorganic substances.
The only cases in which muscle tissue concentrations of inorganic
substances were not homogeneous among study areas were for copper in English
sole muscle tissue, and lead and mercury in crab tissue. Areas of elevated
copper concentrations in English sole muscle (Ruston-Pt. Defiance Shoreline,
Sitcum and St. Paul Waterways) also displayed elevated copper levels in
sediments (>10 times the reference level). English sole from other areas
with high sediment copper levels (e.g., Middle Waterway) showed no evidence
of muscle tissue bioaccumulation. Fish from Middle Waterway had highly
elevated concentrations of copper in liver tissue, however. Therefore,
there is a good relationship between elevated tissue levels of copper and
corresponding sediment contamination.
The higher lead concentrations in crabs from Sitcum and City Waterways
are consistent with the relatively high sediment lead concentrations in
these areas. City and Sitcum Waterways both had average lead sediment
concentrations about 40 times that of the reference area and were considerably
higher than those of any other waterway.
Mercury tissue concentrations were highest in crabs from Hylebos Waterway.
Although sediment mercury levels were elevated in this area (approximately
3.5 times reference concentrations), the highest overall sediment mercury
concentrations were measured in Middle Waterway. Crabs from Middle Waterway
showed no evidence of excess mercury levels. Therefore, there is no apparent
overall relationship between mercury bioaccumulation by crabs and sediment
contamination.
The overall pattern apparent from the metals data is that organisms
with elevated tissue concentrations were generally collected in areas of
measured sediment contamination. Similarly, organisms with low tissue
metal levels were collected from areas of low sediment contamination.
However, a lack of correspondence is indicated by the occurrence of fish
and crabs with little or no tissue contamination from areas with contaminated
sediments. This relationship is shown in Figure 4.15 for Hylebos Waterway
English sole. In this waterway, lead, mercury, and arsenic were measured
at about 10 times reference levels in the sediments. However, there was
no corresponding evidence of elevated fish muscle tissue levels (i.e.,
<1.5 times reference). Of the metals, copper was the most elevated in
Hylebos Waterway sediments (approximately 19 times reference) and also
displayed a moderate increase in fish muscle tissue (approximately 5.5
times reference).
4.43
-------
mn
-I SOLE MUSCLE
_k
o <
•«-
V/
ISHON3 — UV3
DNOP
• «P
«
SP
DNBP
D(
Hg
?
:BA
n
t
• TCE
•
• HCB
' / HCBD
>^As
Cu
-«
Ph(
PC
jn
B
N
ai
DNBP —
DNOP —
PCP —
TCE
Phen —
Naph
B(a)P —
DCS —
HCB —
HCBD —
TCBD —
Jh B(«
Dl-n-butyl pMt
Di-n-oclyl phth
'enlachloroph
Tetrachloroeth
'henanthrene
Naphthalene
Benzo(a) pyrei
1,2 — dichlore
•lexachlorober
Hexachlorobul
Trichlorobutad
l)P TC
BD
lalate
alate
enol
ene
le
benzeru
zene
adiene
lene
i
10
100
1000
EAR — SEDIMENT
Figure 4.15. Relationship of sediment contamination to bioaccumulation in English
sole in Hylebos Waterway. EAR is the ratio of contaminant concentra-
tions in Hylebos Waterway to those in Carr Inlet.
-------
4.5.2 Organic Substances
As was discussed in Sections 3.2 and 3.6, numerous organic substances
have been detected at elevated concentrations in waterway sediments. Few
organic compounds, however, are bioaccumulated in the muscle tissue of
indigenous fish and crabs. Examples of organic compounds that occur in
some waterway areas at average sediment concentrations greater than 100 times
reference values, yet are not detected in fish or crab muscle tissue include:
high molecular weight PAH, tri- and tetrachlorobutadienes, dibenzofuran,
4-methylphenol, and 2-methylnaphthalene.
The chlorinated compounds hexachlorobenzene and hexachlorobutadiene
were detected at low levels only in English sole from Hylebos Waterway.
Contamination of sediments by these compounds was restricted to Hylebos
Waterway. Therefore, the observed bioaccumulation of hexachlorobenzene
and hexachlorobutadiene corresponded directly to the measured sediment
contamination.
The bioaccumulation of other organic compounds did not display such
clear relationships with levels of sediment contamination. Naphthalene
was significantly elevated in English sole from Milwaukee Waterway and
also occurred at apparently elevated concentrations in fish from City Waterway.
Although these two areas had substantial sediment contamination by naphthalene
(140 and 288 times the reference levels, respectively), fish from other
waterways with high sediment naphthalene levels did not display comparable
tissue accumulation. Naphthalene has a relatively low bioaccumulation
potential and should also be readily metabolized by fishes. The high muscle
tissue levels in English sole from Milwaukee and City Waterways may have
resulted from very recent exposure of the fish to water or sediment-associated
naphthalene.
Phthalates were also significantly elevated in English sole from several
waterway areas. Di-n-butyl phthalate was measured at a relatively high
concentration in Hylebos Waterway fish. However, this compound was not
substantially elevated (i.e., <3 times reference) in the sediments of any
waterway. Bis-2(ethylhexyl) phthalate showed some correspondence between
sediment contamination and bioaccumulation, but an overall pattern was
not clear. For the phthalates in general, high sediment levels did not
reliably predict potential bioaccumulation in fishes. Factors that could
account for the absence of a quantitative relationship include:
• Occurrence of substantial water-mediated uptake
• Failure to identify "hot spots" of sediment contamination
• Documented occurrence of high phthalate levels in Commencement
Bay sediments outside of the waterways.
For the organic compounds, Hylebos Waterway English sole had the most
detected compounds in muscle tissue. Many of the organic compounds also
occurred at or near maximum levels in Hylebos fish. As is indicated in
Figure 4.15, sediment elevations of organic compounds in Hylebos Waterway
ranged from 1 or 2 times reference levels (e.g., pentachlorophenol) to >300
4.45
-------
times reference levels (trichlorobutadienes). Most of the compounds detected
in sediments displayed no elevations in fish muscle tissue, however.
The absence of bioaccumulation of many organic compounds results from
two factors: low bioaccumulation potential and metabolism. Many of the
lower molecular weight compounds detected in the sediments have low empirically
determined bioconcentration factors, and therefore would not be expected
to accumulate to high levels in organism tissues. Examples of this group
of compounds includes pentachlorophenol, dichlorobenzenes, and trichloro-
butadienes. Alternatively, PAH have a high potential for uptake that is
offset by the ability of fishes and Crustacea to rapidly metabolize these
compounds. Experimental evidence indicates that rapid uptake of PAH by
fishes is balanced by a rapid metabolism and excretion of metabolites in
the bile (e.g., Stein et al. 1984; Varanasi and Mai ins 1977).
PCBs displayed substantial accumulations in both sediments and organism
tissues from the study area. Unlike PAH, PCBs are not rapidly metabolized
by organisms and tend to accumulate in tissues. In Commencement Bay waterways,
PCBs occurred in muscle tissue of fishes and crabs at concentrations up
to 10 times reference levels. Similar results have been observed in studies
of Los Angeles harbor where, although sediments are contaminated by both
PCBs and PAH, resident fishes only show evidence of PCB bioaccumulation
(Gossett et al. 1983).
PCBs were subjected to more detailed evaluations of sediment-tissue
relationships because of their occurrence throughout the study area and
their relative health hazard. A comparison of elevations above reference
for PCBs in sediments and English sole muscle tissue is presented in Figure
4.16. For Commencement Bay waterways, increasing tissue PCB levels generally
corresponded with increasing sediment contamination. St. Paul Waterway
did not fit this trend (i.e., there was no evidence of elevated bioaccumulation
although sediments appeared to be contaminated). Examination of the sediment
data for St. Paul Waterway indicated that, due to laboratory problems,
PCBs were undetected at five of the six stations. For these cases, the
analytical detection limits for PCBs were exceptionally high (90-180 ug/kg).
Thus, the apparently high sediment PCB concentrations resulted from an
average of several high detection limit values that were used as a conservative
estimate of the maximum potential concentration of PCBs. This data problem
was limited to the five stations in St. Paul Waterway. Because of the
uncertainty in the levels of sediment PCBs in that area, the St. Paul Waterway
data were excluded from statistical analyses of the sediment-tissue relation-
ships.
Statistical analyses (Pearson correlation) of the data presented in
Figure 4.16 indicated that PCB elevations in muscle tissue were significantly
correlated (r=0.82, P<0.05) with sediment elevations. This relationship
showed that as sediment PCB levels exceeded 10 times reference (>60 ug/kg),
the sole muscle tissue concentrations were approximately 10 times reference
or greater (>360 ug/kg wet weight). Bioaccumulation of PCBs to such levels
in seafood organisms would result in a substantial risk to individuals
eating relatively large amounts of locally caught seafood (see Section 5).
4.46
-------
100
HI
o
00
5
HI
o
co
I
CO
_i
O
UJ
EAR
_i
O
1.0
• THIS STUDY
A HISTORICAL DATA
BL-
SI
Ml
Cl
MD
•is
HY
1.0
10
EAR — SEDIMENT
# SEE DETECTION LIMIT DISCUSSION IN TEXT
100
Figure 4.16.
Relationship of PCB contamination of sediments
and fish muscle tissue for Commencement Bay
waterways.
4.47
-------
4.5.3 Summary
There were no generalized quantitative relationships between metals
concentrations in sediments and in fish tissues. These results are consistent
with the ability of fishes to regulate metals, especially in muscle tissue.
For organic substances, there were apparent relationships between sediment
and tissue levels of chlorinated compounds. For PCBs, substantial bio-
accumulation to concentrations about 10 times reference levels occurred
at average sediment concentrations exceeding 60 ug/kg.
4.6 RELATIONSHIP BETWEEN BIOACCUMULATION AND FISH HISTOPATHOLOGY
This section examines the relationship between tissue contamination
in English sole and the occurrence of hepatic lesions. The primary objective
is to determine whether there are relationships between the accumulation
of contaminants in liver tissue and the presence of liver abnormalities
such as neoplasms or megalocytic hepatosis. The occurrence of such relation-
ships could then be used to identify possible causative agents in hepatic
diseases of fishes and to identify problem contaminants in the study area.
4.6.1 Inorganic Substances
Data for several inorganic constituents in fish liver samples did
not pass the project quality control checks and were therefore considered
to be of questionable quality. Data quality problems were associated with
high variability of replicate samples and lack of accuracy for a bovine
liver standard. Questionable data existed for arsenic, chromium, lead,
and selenium.
Liver composite concentrations for metals with acceptable data are
presented in Table 4.13. Data are presented for normal and abnormal liver
composites to enable comparisons of inorganic contaminant concentrations
among study areas and to evaluate whether increased contaminant levels
are associated with hepatic lesions. Concentrations of the five metals
(cadmium, copper, nickel, zinc, and mercury) were very similar among normal
English sole liver samples from Carr Inlet, the Ruston-Pt. Defiance Shoreline,
and the waterways. Although not presented in Table 4.13, liver concentrations
of these metals were similarly consistent among normal English sole from
individual waterways.
Concentrations of cadmium, nickel, mercury, and zinc in abnormal liver
composites were also similar among lesion categories and were similar to
concentrations in normal livers. Therefore, for these metals there is
no evidence of differential bioaccumulation relative to study area or to
health of the fish.
Copper concentrations were similar among sample groups except_for
a considerably elevated average concentration in the fish with various
hepatic abnormalities from the Commencement Bay waterways (Table 4.13).
Examination of the data indicated that this elevation was entirely the
result of a very high copper concentration (189 mg/kg wet weight) in the
abnormal liver sample from Middle Waterway. Normal English sole livers
from Middle Waterway had a copper concentration of 4.4 mg/kg wet weight,
4.48
-------
TABLE 4.13. AVERAGE METAL CONCENTRATIONS (mg/kg wet weight)
IN ENGLISH SOLE COMPOSITE LIVER SAMPLES
Liver
Condition
Normal
Normal
Normal
Neoplasms
Megalocytic
hepatosis
Multiple
lesions
Various
abnormal ities
Location
Waterways
Carr Inlet
Ruston-Pt.
Defiance
Waterways
Waterways
Waterways
Waterways
n
12
2
3
1
3
4
4
Cadmium
0.42
0.41
0.56
0.21
0.37
0.46
0.48
Copper
5.1
7.2
10.1
3.4
5.5
5.9
51
Nickel
0.40
0.39
0.46
0.23
0.60
0.69
0.72
Zinc
19.9
24.6
25.3
21.0
15.0
19.0
22.2
Mercury
0.075
0.060
0.097
0.088
0.086
0.098
0.106
4.49
-------
which was similar to those from Carr Inlet (7.2 mg/kg wet weight). Middle
Waterway sediments had the highest copper concentrations among the waterways.
These data suggest that fish with hepatic lesions in Middle Waterway are
accumulating excess levels of copper in their livers.
4.6.2 Organic Substances
Analyses of nonvolatile organic compounds in English sole liver composites
resulted in few compounds being detected. Detection limits for these compounds
typically ranged from 25 to 100 ug/kg wet weight, although detection limits
for pesticides ranged from 100 to 200 ug/kg wet weight. Detected compounds
included phenol, naphthalene, hexachlorobenzene (HCB), hexachlorobutadiene
(HCBD), di-n-butyl phthalate, benzyl alcohol, and PCBs. In the 35 samples,
phenol and di-n-butyl phthalate were detected only twice each, with no
apparent relationship to liver condition. HCB (130-260 ug/kg wet weight)
and HCBD (71-170 ug/kg wet weight) were detected only in fish livers from
Hylebos Waterway. Each of these compounds was detected at similar concen-
trations in both normal and diseased liver samples from Hylebos Waterway.
Naphthalene was detected at concentrations of 30-240 ug/kg wet weight
only in normal livers from Carr Inlet and several waterways. Benzyl alcohol
was detected in 12 of the 35 samples at concentrations of 220 to 14,000 ug/kg
wet weight.
Of the organic compounds, PCBs were the most frequently detected (all
35 samples) and were measured at the highest concentrations, ranging from
220 to 11,000 ug/kg wet weight (Table 4.14). When compared to concentrations
from Carr Inlet, PCBs were clearly elevated in both normal and diseased
livers from English sole in Commencement Bay waterways. Average concen-
trations in both diseased and normal livers from the waterways were typically
about 2,000 ug/kg wet weight. Fish with normal livers, megalocytic hepatosis,
neoplasms, and various other abnormalities all had similar PCB levels in
their livers. Fish with multiple hepatic lesions from the waterways had
the highest average (4,500 ug/kg wet weight) and maximum (11,000 ug/kg
wet weight) liver PCB concentrations. Normal English sole collected from
the Ruston-Pt. Defiance Shoreline had liver PCB levels that were intermediate
between those measured in fish from the waterways and those from Carr Inlet.
These data indicate that sole in the waterways are accumulating higher
levels of PCBs in their livers relative to reference levels in Puget Sound.
Relatively high concentrations (about 2,000 ug/kg wet weight) were consistently
measured in both normal and abnormal livers. Although the highest PCB
levels occurred in fish with multiple hepatic lesions, there is no overall
indication of higher PCB concentrations in livers of diseased fish.
The relationship between tissue contamination and fish histopathology
was investigated further by evaluating the occurrences of liver lesions
in the 85 English sole used for muscle tissue bioaccumulation studies.
As was indicated in Section 3.6, few contaminants displayed elevated concentra-
tions relative to reference conditions in Commencement Bay sole muscle
samples. Moreover, several of the detected organic compounds were found
at low levels in only a few fish from selected sites. PCBs, however, were
detected in almost all English sole tested and were significantly elevated
in several Commencement Bay waterways. PCBs also pose the greatest public
4.50
-------
TABLE 4.14. TOTAL PCB CONCENTRATIONS (ug/kg wet weight) IN ENGLISH
SOLE COMPOSITE LIVER SAMPLES
Liver
Condition
Normal
Normal
Normal
Neoplasms
Megalocytic
Hepatosis
Multiple
Lesions
Various
Abnormal ities
Location
Waterways
Carr Inlet
Ruston-Pt.
Defiance
Waterways
Waterways
Waterways
Waterways
n
12
2
3
1
3
4
4
Mean
2,012
260
866
1,800
1,990
4,500
1,925
Range
1,000-4,600
220-300
620-1,037
—
970-2,900
1,900-11,000
1,100-3,000
4.51
-------
health risk of the contaminants bioaccumulated by Commencement Bay English
sole. Therefore, data on PCB levels in muscle tissue were compared with
liver histopathology results to determine whether muscle tissue from fish
with liver lesions also had elevated contaminant levels.
The 75 English sole collected from Commencement Bay for bioaccumulation
studies are categorized according to the occurrence of major hepatic lesion
types in Table 4.15. For preneoplastic lesions and megalocytic hepatosis,
lesion prevalences were lower in fish with muscle tissue PCB concentrations
<100 ug/kg wet weight than in fish with PCB levels >100 ug/kg wet weight.
However, statistical analyses using the G-test of all tTTree lesion categories
indicated that lesion prevalence was independent (P>0.05) of PCB levels.
Thus, there is no clear relationship between uptake of PCBs and occurrence
of liver lesions. English sole with all three major lesion types can have
either low or high PCB concentrations in their muscle tissue.
Although aromatic hydrocarbons have been implicated as causative agents
in the development of fish hepatic lesions (Mai ins et al. 1984), these
compounds are rapidly metabolized and do not generally accumulate in fish
muscle tissue. In this study, naphthalene was the only aromatic hydrocarbon
measured at detectable levels in English sole muscle. Naphthalene was
detected relatively infrequently and occurred consistently in high concentra-
tions only in four English sole from Milwaukee Waterway. Therefore, the
naphthalene data were not appropriate for statistical analyses of disease
prevalence. Qualitative examination of the histopathological data indicates,
however, that two of the four English sole from Milwaukee Waterway with
high naphthalene concentrations also had megalocytic hepatosis. One of
these sole also had hepatic neoplasms and preneoplastic lesions.
4.6.3 Summary
There were no generalized patterns of higher levels of contaminants
in fish livers with serious lesions when compared to normal livers. Although
fish with multiple hepatic lesions had the highest liver concentrations
of PCBs, substantially elevated PCB levels occurred in both normal and
abnormal livers in English sole from the waterways.
4.52
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TABLE 4.15. OCCURRENCES OF MAJOR HEPATIC LESIONS RELATIVE TO MUSCLE
TISSUE PCB LEVELS IN ENGLISH SOLE FROM COMMENCEMENT BAY
Lesion Category
Muscle Megalocytic
PCB Concentration Neoplasm Preneoplastic Hepatosis
(ug/kg wet weight) Yes No Yes No Yes No
<100
100-399
MOO
1
0
1
31
30
12
3
5
2
29
25
11
1
5
2
31
25
11
4.53
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5. PUBLIC HEALTH ASSESSMENT
5.1 INTRODUCTION
The results of this study and previous investigations have shown that
various inorganic and organic contaminants are bioaccumulated by Commencement
Bay fishes and shellfish. The objective of the public health assessment
is to determine if there are significant health risks associated with con-
sumption of fish and shellfish from Commencement Bay. This assessment
used data on tissue concentrations of contaminants collected in 1984 as
part of the bioaccumulation studies (see Section 3.6) and data on fish
catch/consumption from a 1981 survey by the Tacoma-Pierce County Health
Department.
Only one exposure route (i.e., eating non-salmonid fish, fish livers,
and crabs from Commencement Bay) was considered in the assessment. Other
possible exposure routes (e.g., drinking water, inhalation) were not considered.
English sole and crab were selected for these analyses because of
their availability in the project area and because they live in close asso-
ciation with contaminated bottom sediments. Although English sole are
not commonly caught by local fishermen, they were used as a conservative
estimate of the maximum contaminant levels that would be expected to occur
in edible fish tissues. Data from a previous study (Gahler et al. 1982)
have shown that concentrations of PCBs and arsenic are two to three times
higher in English sole than in commonly caught fish such as walleye pollack,
hake, and cod.
The remainder of this section is a summary of the assessment of human
health risks conducted for the Commencement Bay study. The detailed results
are contained in a separate report prepared under the Commencement Bay
project (Versar, Inc. 1985).
5.2 SUMMARY OF RESULTS
As indicated in Section 3.6, English sole and crabs from Commencement
Bay contained higher concentrations and a wider variety of organic compounds
than conspecifics from the Carr Inlet reference area. There was little
difference between Commencement Bay and Carr Inlet in the concentrations
of metals in fish and crab tissues.
Risk assessments for carcinogens and noncarcinogens were based on
the range of fish consumption rates presented in Section 2.11. Of the
total exposed population of 15,220 persons, only 30 persons experienced
the maximum consumption rate of 1 Ib/day. From the same population, 1,735
persons consumed 1 Ib/mo. Approximately 82 percent of these exposed population
(12,500 persons) consumed less than 1 Ib/mo.
In subsequent discussions, individual carcinogenic risks are presented
as a probability of contracting cancer resulting from the specified exposure.
5.1
-------
These risks are presented as negative exponents, where, for example, 10"6
represents a 1 in 1 million chance of contracting cancer.
5.2.1 Carcinogens in Fish Muscle Tissue
At the maximum fish consumption rate of 1 Ib/day, estimated individual
lifetime risks would exceed 10'6 for six carcinogens (Table 5.1: PCBs,
arsenic, hexachlorobenzene, hexachlorobutadiene, bis(2-ethylhexyl) phthalate,
and tetrachloroethene. At this high consumption rate, individual risks
would range from 10~5 to 10~3. At a fish consumption rate of 1 Ib/mo,
only PCBs and arsenic would exceed the 10~6 risk level.
For a given consumption rate, estimated individual risks from consuming
Commencement Bay fish muscle would exceed those for consuming Carr Inlet
fish for three of the above six carcinogens: PCBs, bis(Z-ethylhexyl) phthalate,
and tetrachloroethene. Comparative risks for these compounds at the maximum
1 Ib/day consumption rate are:
Individual Risk
Chemical Commencement Bay Carr Inlet
PCBs 6x10-3 IxlO-3
bis(2-ethylhexyl) phthalate 2x10-5 3xlO~6
Tetrachloroethene 1x10-5 3xlO~6
Estimated individual risks from consuming fish from Commencement Bay
and Carr Inlet for arsenic were similar, although Carr Inlet risks were
slightly higher. At the maximum 1 Ib/day ingestion rate, risks for arsenic
would be: Commencement Bay, 4xlO"4; Carr Inlet, 7xlO"4.
Hexachlorobutadiene and hexachlorobenzene were detected in 2 of 15
English sole analyzed in Hylebos Waterway, but not in other areas. These
compounds were present in the two Hylebos Waterway fish at concentrations
near the lower limit of analytical detection. The estimated risk from
eating these two fish was similar to the risk from eating fish from Carr
Inlet since it was assumed that all contaminants were present in concentrations
equal to the detection limit. Hylebos Waterway remains unique, however,
with respect to the presence of these two chemicals.
Fish tissue concentrations and hence the associated risk for consuming
fish varied somewhat among the Commencement Bay Waterways. For PCBs, the
suspected carcinogen representing the greatest individual risk, fish consumed
from City and Hylebos Waterways represented the greatest risk. For PCBs,
risks associated with eating fish from Hylebos and City Waterways were
about 10 times higher than those for fish from Carr Inlet. Risks associated
with PCBs decreased with distance from City Waterway towards Pt. Defiance.
Estimated individual risks for all chemicals in the Pt. Defiance area
were similar to those in the Carr Inlet reference area. For arsenic, the
risks were similar throughout the project area at the reference area.
Estimated risks for bis(2-ethylhexyl) phthalate ranged from 2x10-5 (City,
Milwaukee, Ruston-Pt. Defiance Shoreline) to 3xlO"6 fHylebos Waterway and
Carr Inlet) at the 1 Ib/day consumption rate. Tetrachloroethene was only
analyzed for in four areas. At the maximum consumption rate, estimated
risks would range from 2x10-5 (St. Paul, Hylebos) to 3x10-6 (Carr Inlet).
5.2
-------
TABLE 5.1. ESTIMATED INDIVIDUAL LIFETIME RISKS
FOR ORGANIC COMPOUNDS IN FISH MUSCLE TISSUE
Chemical
1
Consumption Rate
Ib/day 1 1
1 Ib/mo
2x10-4
PCB
Arsenic
Hexachlorobenzene
Hexachlorobutadiene
bis(Z-ethylhexyl) phthalate
Tetrachloroethene
6x10-3
4x10-4
1x10-4
2x10-5
2x10-5
1x10-5
4xlO-6
7x10-7
6x10-7
5x10-7
5.3
-------
Hexachlorobutadiene and hexachlorobenzene were detected in fish muscle
tissue only in Hylebos Waterway.
Estimated individual risks for two carcinogens found in the sediments
but not detected in fish muscle tissue would exceed 10~6 under the conservative
assumption that the compounds are present in fish muscle tissue at the
detection limit: polynuclear aromatic hydrocarbons (PAH) and n-nitrosodi-
propylamine. At the 1 Ib/day consumption rate, individual risks associated
with these compounds would range from 3 to 4xlO"3. However, neither compound
would be expected to be present in fish muscle tissue at concentrations
near the detection limit.
A primary objective of the Commencement Bay project was to determine
if any fish tissue contaminant resulted in the prediction of one or more
excess cancer cases in the exposed population. This assessment was accomplished
by applying the individual risks for each carcinogen to the exposed population
estimated from the catch/consumption survey (see Section 2.11). The highest
estimated incidence of cancer in the exposed population of 15,220 persons
was between one and two cases in 70 years, attributable to PCBs causing
cancer of the liver (Table 5.2). All available data indicate that the
chemical associated with the highest individual lifetime cancer risk is
PCBs; the next highest risk is attributable to arsenic. The maximum predicted
cancer cases attributable to the two chemicals over a 70-yr exposure period
are indicated in Table 5.2. Only for PCBs did the predicted number of
cases exceed one, even with the conservative approach taken in this assessment
(continuous exposure for 70 yr, etc.). As arsenic exposure is predicted
to result in fewer than one case in 70 yr, and it ranked the second highest
in individual risk, no other chemical is expected to produce cancer in
the exposed population under the circumstances presented in this assessment.
5.2.2 Noncarcinogens in Fish Muscle Tissue
Three chemicals were present in fish muscle at levels that would cause
exposure to exceed the Acceptable Daily Intake (ADI) at the 1 Ib/day consumption
rate: antimony, lead, and mercury.
Tissue concentrations of these chemicals were very similar among project
areas and at the Carr Inlet reference site. Therefore, the ADIs would
be exceeded at both Carr Inlet and Commencement Bay for the 1 Ib/day consumption
rate.
Limiting consumption of fish to one-half pound per day would result
in exposure less than the ADI for all of these chemicals. However, health
risks at this consumption rate would still exist due to the presence of
carcinogens.
5.2.3 Carcinogens in Crab Muscle Tissue
For PCBs and arsenic, estimated individual risks from consuming crabs
from Commencement Bay were approximately the same as those from eating
fish. Bis(2-ethylhexyl)phthalate represented a higher risk in crabs than
in fish. Average risks for Commencement Bay, based on a consumption rate
of 1 Ib/day of crab muscle, would be as follows:
5.4
-------
TABLE 5.2. PROJECTED LIFETIME CANCER CASES
FOR PCBs AND ARSENIC
Consumption
Frequency
(1 Ib)
PCBs
Daily
Weekly
Monthly
Bimonthly
Twice/yr
Yearly
TOTAL
Arsenic
Daily
Weekly
Monthly
Bimonthly
Twice/yr
Yearly
Fish
Intake
(g/day)
453.0
64.7
15.1
7.4
2.5
1.2
453.0
64.7
15.1
7.4
2.5
1.2
Exposure
(mg/kg/day)
1.36x10-3
1.94xlO"5
4.53x10"^
2.22x10"=
7.50x10-°
3.60xlO"6
3.16x10"^
4.51x10"°
1.05x10"?
5.16x10";
1.74x10";
8. 37x1 O"8
Individual
Risk
5.90xlO"5J
8.42x10"*
1.97x10":
9.63x10"=
3.26x10"=
1.56xlO"5
4.42x10"*
6.31x10 ;?
1.47x10"=
7.22x10"°
2.44x10"°
1.17xlO"b
Exposed
Population
30
1,005
1,735
1,111
2,618
8,721
15,220
30
1,005
1,735
1,111
2,618
8,721
Predicted
Cancer
Cases
0.18
0.85
0.34
0.11
0.09
0.14
1.69
0.01
0.06
0.03
0.01
0.01
0.01
TOTAL
15,220
0.13
5.5
-------
PCBs 3x10-3
Arsenic 2x10-4
Bis(2-ethylhexyl)phthalate 3x10-6
Risks for all other carcinogens were less than 10"6. Only PCBs resulted
in average individual risks from eating Commencement Bay crabs that were
greater than the risks from eating Carr Inlet crabs. The average risk
for Commencement Bay crabs due to PCBs was about three times the Carr Inlet
risk. Within Commencement Bay, highest PCB risks were for crabs from Sitcum
Waterway. The risks associated with bis(2-ethylhexyl) phthalate were higher
from eating Carr Inlet crabs than Commencement Bay crabs.
5.2.4 Noncarcinogens in Crab Muscle^
At the maximum consumption rate of 1 Ib/day, calculated exposures
would exceed the ADI for the following contaminants: antimony, lead, silver,
zinc, and mercury. For these metals, the ADIs were exceeded for crabs
from both Commencement Bay and Carr Inlet. For most of the metals, the
differences between Carr Inlet and Commencement Bay were slight. The maximum
difference between Commencement Bay and the reference area was for lead,
where crabs from Sitcum Waterway exceeded the ADI by a factor of 4.2.
Limiting consumption of crabs from either Commencement Bay or Carr
Inlet to 1 Ib/wk or less would result in all noncarcinogenic exposures
being below the ADI.
5.2.5 Consumption of Fish Livers
Twenty-one chemicals were detected in at least one fish liver composite
sample from Commencement Bay. Four of the detected chemicals are considered
to be carcinogens: PCBs, hexachlorobenzene, hexachlorobutadiene, and arsenic.
At the maximum consumption rate of 0.12 Ib/day, consumption of PCBs
in fish liver resulted in a predicted individual lifetime risk of 2xlO"2.
This risk is higher than the corresponding risk from consuming PCBs in
fish muscle tissue (6xlO~3) because of the much higher PCB levels in fish
liver. The predicted risk level for PCBs in Commencement Bay fish livers
is also about 15 times higher than the corresponding risk for fish livers
from Carr Inlet.
Maximum predicted carcinogenic risks for hexachlorobenzene and hexachloro-
butadiene in fish liver were about the same as the corresponding risks
for fish muscle (10"4 and 10"5, respectively). All other predicted carcinogenic
risks were much lower than these levels.
These maximum predicted risks are associated with a high assumed con-
sumption rate (i.e., eating almost 2 oz of liver every day). The predicted
risks would be much lower for less frequent consumption of fish livers.
This worst-case scenario was used, however, because of the absence of available
information on fish liver consumption for Commencement Bay.
The ratios of exposure to ADI for all noncarcinogens present in fish
livers from Commencement Bay were less than 0.1. Therefore, even at the
5.6
-------
maximum consumption rate of 0.12 Ib/day, no human health effects attributable
to these chemicals would be expected.
Of the chemicals detected in fish livers from Commencement Bay, PCBs
pose the greatest potential risk to public health. Although the maximum
predicted risk (10~2) Was associated with a high consumption rate, even
much less frequent consumption of fish liver would result in a substantial
predicted risk.
5.7
-------
6.0 PRIORITIZATION OF PROBLEM AREAS AND CONTAMINANTS
6.1 INTRODUCTION
Results from previous sections on chemistry, toxicity, and biological
effects are integrated in this section to identify and prioritize problem
areas for source evaluation. The decision-making approach for the ranking
of problem areas is presented in detail in Tetra Tech (1984a) and summarized
in Figure 6.1. The first step of this procedure was to assemble "action
assessment" matrices of the independent indicators used to characterize
Commencement Bay sediments and biota. These data were compared among areas
and evaluated for:
• The significance of each indicator relative to reference
conditions
• The combination of significant indicators that characterized
each area
• The relative magnitudes of significant indicators.
Two levels of spatial resolution of contaminant effects were provided
by these matrices. First, average conditions were compared among the eight
Commencement Bay study areas (i.e., the seven waterways and the Ruston-
Pt. Defiance Shoreline). Second, average conditions were compared among
segments within study areas to define general trends in the larger areas
(Hylebos, Blair, and City Waterways, and the Ruston-Pt. Defiance Shoreline).
Action-level guidelines were then applied to identify and rank study areas
and segments of concern. A widespread problem or a "hot spot" of major
significance occurred within each study area or segment of concern.
Using all available data [including acceptable historical data and
data from the quantitative relationships (Section 4)] the spatial extent
of each problem area was then defined. "Hot spots" of strictly local signifi-
cance that were not reflected in average conditions at the study area or
segment level were also defined. Problem areas were then ranked according
to severity of observed contamination, toxicity, and biological effects.
Potential problem chemicals were also identified and ranked. On the basis
of these rankings, potential sources of characteristic chemicals in each
problem area were evaluated (Section 7). Finally, priorities for remedial
action were recommended (Section 8), based on the relative magnitude of
problems, the spatial extent of the problem area, and the degree of confidence
that sources of potential problem chemicals had been identified.
6.2 IDENTIFICATION OF PROBLEM AREAS
6.2.1 Action Assessment Matrices
The initial identification of problem areas was conducted using an
action assessment matrix (Table 6.1). Average elevation above reference
(EAR) values for different indicators of sediment contamination, sediment
6.1
-------
ASSEMBLE ACTION ASSESSMENT
MATRICES
APPLY ACTION LEVEL GUIDELINES
IDENTIFY STUDY AREAS AND
SEGMENTS OF CONCERN
O
U
A
N
T
I
T
A
T
I
V
E
R
E
L
A
T
I
O
N
S
H
I
P
S
RANK STUDY
AREAS AND
SEGMENTS
(AVERAGE
CONDITIONS)
AND
H
I
S
T
O
R
I
A
L
>
DEFINE EXTENT OF
PROBLEM AREAS WITHIN
STUDY AREAS AND SEGMENTS
RANK PROBLEM AREAS
(WORST CONDITIONS)
I
>
IDENTIFY POTENTIAL
PROBLEM CHEMICALS IN
PROBLEM AREAS
I I
RANK PROBLEM CHEMICALS
CONDUCT SOURCE EVALUATIONS
FINAL PRIORITIZATION OF
PROBLEM AREAS FOR
REMEDIAL ACTION
Figure 6.1. Evaluation and prioritization of problem areas
and chemicals.
6.2
-------
TABLE 6.1. ACTION ASSESSMENT MATRIX OF SEDIMENT CONTAMINATION, SEDIMENT TOXICITY,
AND BIOLOGICAL EFFECTS INDICES FOR COMMENCEMENT BAY STUDY AREAS
STUDY
VARIABLE Hylebos Blair
SEDIMENT CHEMISTRY
Sb
As
Cd
Cu+Pb+Zn
Hg
Ni
Phenol
Pentachl orophenol
LPAH
HPAH <
Chlor. benzenes
Chlor. butadienes
Phthalates
PCBs
4-Methyl phenol
Benzyl alcohol
Benzoic acid
Dibenzofuran
Nitrosodiphenylamine
Tetrachloroethene
SEDIMENT TOXICITY
Amphipod bioassay
Oyster bioassay
INFAUNA0
Total benthos
Polychaetes
Molluscs
Crustaceans
10.
12.
2.4
10.
8.1
1.4
< 6.4
1.7
<45.
120.
9.9
130.
4.0
<48.
<7.3
5.0
< 0.7
29.
2.1
12.
2.1
2.2
1.2
0.6
^W
4.0
l!9
4.8
< 3.7
0.7
< 5.2
< 2.3
<28.
<42.
< 4.4
<12.
< 2.2
< 3.2
25.
< 2.4
< 0.6
1.9
1.0
1.0
1.0
1.0
Site urn
8.0
11.
2.8
24.
5.0
0.6
4.3
< 2.1
<68.
<65.
2.6
|< 2.4 |
< 0.58
10.
2.4
< 0.5
73.
< 7.3
U 1.0
0.7
0.4
1.4
AREA
Milwaukee
3.6
3.6
1.7
3^8
0.8
<60.
<68.
< 2.5
< 1.2
< 0.66
13.
3.4
< 0.7
u i!o
L4
0.8
0.7
1.1
0.4
ELEVATIONS3
St. Paul Middle City Ruston
4.2
2.2
1.7
5.5
5.1
0.8
U l'.9
<73.
<27.
< 1.8
< 1.3
< 0.56
L300.
< 6.7
< 1.0
1 52.
U 1.2
U 1.0
1 4.8
3.8
1.9
1.5
1 6.8
1.0
1
9.3
9.6
2.8
18.
26.
0.7
11.
5.6
<110.
< 97.
< 6.1
< 6.8
< 5.1
8.5
< 33.
3.3
U 0.1
< 1.0
1.4
1.8
1.5
0.7
5.4
4.6
7.0
7.5
5.5
22.
10.
1.4
9.4
< 1.9
<120.
<140.
< 9.0
< 1.9
< 7.1
<12.
30.
4.7
< 1.6
58.
14.
U 1.0
2.7
2.6
0.7
0.8
U2
510.
620.
27.
120.
160.
2.8
4.5
< 1.0
<87.
<85.
< 3.3
< 1.7
4.5
19.
<10.
< 1.2
< 0.5
<160.
<22.
3.9
2.2
0.6
0.5
1.2
0.7
REFERENCE
VALUED
110. ppb
3370. ppb
950. ppb
35000. ppb
40. ppb
1740. ppb
< 33 ppb
U 33. ppb
< 41. ppb
< 79. ppb
U 21. ppb
U 62. ppb
< 280. ppb
< 6.0 ppb
< 13. ppb
U 10. ppb
< 140. ppb
U 3.7 ppb
U 4.1 ppb
U 10. ppb
9.3 S
13.0 X
d
d
d
d
FISH PATHOLOGY
Lesion prevalence
FISH BIOACCUMULATION
2.7
1.7
2.1
6.7
Copper
Mercury
Naphthalene
Phthalates
PCBs6
DDE
5.6
1.5
21.
9.2
3.8
1.0
0.93
0.41
11.
7.0
5.1
1 4.0 | 2
0.80 1
0.33 24
0.53 3
f 4.8 | 2
3 | 9.1 I 1.0 3
6 0.76 1.3 0
0.19 0.19 4
.6 0.41 0.41 6
.8 1.1 4.7 9
.4 1.7 1.7 6
.8 I 2.5 |
.82 0.96
.1 0.19
.7 5.6
.8 1.9
.2 2.9
U 38. ppb
U 55. ppb
< 54. ppb
< 74. ppb
< 36. ppb
< 1.8 ppb
8 Boxed numbers represent elevations of chemical concentrations that exceed all Puget Sound reference area values,
and statistically significant toxicity and biological effects at the P<0.05 significance level compared with reference
conditions. The "U" qualifier indicates the chemical was undetected and the detection limit is shown. The "<" qualifier
indicates the chemical was undetected at one or more stations. The detection limit is used in the calculations.
I* Elevation above reference (EAR) values shown for each area are based on Carr Inlet reference values for each variable
except for benthos (see footnote d).
c Infauna EAR are based on the elevation in biological effects represented by reductions in infaunal abundances
relative to reference conditions. EAR for all other variables reflect an increase in the value of the variable at
Commencement Bay compared with reference conditions.
<* See Table 6.7 for a summary of reference benthic values used for groups of stations with similar grain size.
e Locations where PCB concentrations are significantly elevated also pose a significant health risk to the exposed
population (see Table 6.8 guidelines).
6.3
-------
toxicity, and biological effects (i.e., infaunal abundance, and English
sole histopathology and muscle bioaccumulation) are summarized for each
study area in Table 6.1. Reference values are also presented. Indicators
are defined in the decision-making approach document (Tetra Tech 1984a).
Original values for an indicator can be obtained by multiplying the EAR
reported in the table by the appropriate reference value. Similar data
averaged over study area segments in Hylebos, Blair, and City Waterways,
and the Ruston-Pt. Defiance Shoreline are summarized in Tables 6.2-6.5.
Waterway segments are arranged from the mouth (left) to the head (right).
Ruston-Pt. Defiance Shoreline segments are arranged from Pt. Defiance (left)
to the eastern shoreline off City Waterway (right). Histopathology and
bioaccumulation data for English sole are not presented in these latter
matrices, but are used only when averaged over an entire study area to
indicate broad-scale biological effects. Mean reference values used to
calculate benthic infauna EAR are presented in Table 6.6. These values
differed among study areas and segments because of the grain size differences
summarized in Table 6.7.
The average concentration of several organic compounds was significant
i.e., exceeded all Puget Sound reference conditions) in all study areas
Figure 6.1). Average metals contamination was significant in all areas
except St. Paul Waterway. Blair and Milwaukee Waterways had the least
chemical contamination, based on number and magnitude of significantly
elevated chemical indices. Average sediment toxicity was statistically
significant (P<0.05 experimentwise, t-test) in all areas except Middle
Waterway. Average toxicity, as indicated by both kinds of bioassay, was
significantly elevated only in Hylebos and City Waterway study areas.
Elevations of benthic effects, as indicated by depressions abundances,
were statistically significant (P<0.05 experimentwise, t-test) in Hylebos,
Sitcum, St. Paul, Middle, and City Waterway.
The average prevalence of lesions (discussed in Section 3.5.6) was
statistically significant (P<0.05 experimentwise, 2x2 contingency test)
in all study areas except St. Paul and City Waterways, and the Ruston-Pt.
Defiance Shoreline. Bioaccumulation in English sole muscle tissue was
statistically significant (P<0.05) in all study areas except Middle Waterway.
The largest number of significant indicators was observed in Hylebos
Waterway (significant EAR for 18 chemicals or groups of chemicals, and
seven toxicity or biological effects indicators). The lowest number of
significant indicators averaged over a study area was found in St. Paul
Waterway (significant EAR for eight chemicals or groups of chemicals, and
three significant toxicity or biological effects indicators).
Contamination, toxicity, and benthic effects were heterogeneous within
the larger study areas (Tables 6.2-6.5). For example, although Hylebos
Waterway as a whole exhibited the largest number of significant indicators
and chemical contamination was evident throughout the waterway, there was
no significant toxicity in Segments HYS3 or HYS4 and no significant benthic
effects in Segments HYS3 or HYS6. In general, chemical contamination in
Hylebos Waterway was most extensive at the head of the waterway, with additional
6.4
-------
TABLE 6.2. ACTION ASSESSMENT MATRIX OF SEDIMENT CONTAMINATION, SEDIMENT TOXICITY,
AND BIOLOGICAL EFFECTS INDICES FOR COMMENCEMENT BAY STUDY AREAS
H Y L
VARIABLE HY-6
SEDIMENT CHEMISTRY
Sb |10. |
As 4.9
Cd | 2.5 |
Cu+Pb+Zn 4.3
Hg 3.1
Ni 0.7
Phenol 5.9
Pentachlorophenol < 2.1
LPAH <19.
HPAH <19.
Chlor. benzenes < 2.9
Chlor. butadienes <11.
Phthalates <11.
PCBs <10.
4-Methyl phenol j5_
Benzyl alcohol 6.4
Benzoic acid < 0.6
Dibenzofuran | 14. I
Nitrosodiphenylamine U 1.2
Tetrachloroethene —
SEDIMENT TOXICITY
Amphipod bioassay 1.7
Oyster bioassay I 2.0 |
INFAUNAC
Total benthos 0.6
Polychaetes 0.4
Molluscs 0.8
Crustaceans 0.3
E B 0 S
HY-E
4.5
i.'e
7.8
11.
1.2
< 4.7
< 1.8
<43.
<58.
16.
<290.
< 2.6
I <49.
< 4.6
< 5.3
< 0.6
I 33.
< 1.4
| < 1.8
2.4
1.9
1.2
0.6
1 4.7
1.7
S
E G M
HY-4
6.8
7.0
2.0
7.8
7.0
1.1
3.4
< 2.4
<52.
<99.
< 7.6
110.
< 2.1
pltT"
18.
3.5
< 0.5
34.
< 6.8
—
2.1
1.8
3.5
1.4
44.
14.
E N T E L E
HY-3
8.3
2!o
10.
6.6
1.4
1< 5.01
<0.98
<27.
<68.
< 5.9
1 55. 1
< 1.5
< 4.6
< 3.0
< 0.6
18.
< 3.5
3.3
0.9
1.8
0.7
0.3
4.4
0.7
VAT
HY-2
8.2
19.
3.1
14.
8.0
2.3
< 4.4
U 1.7
<73.
<220.
< 6.8
80.
< 6.3
110.
< 5.0
< 9.8
< 1.5
1 42.
U 1.2
2.2
2.7
2.5
27
-------
TABLE 6.3. ACTION ASSESSMENT MATRIX OF SEDIMENT CONTAMINATION, SEDIMENT TOXICITY,
AND BIOLOGICAL EFFECTS INDICES FOR COMMENCEMENT BAY STUDY AREAS
BLAIR SEGMENT
VARIABLE BL-S4 BL-S3
SEDIMENT CHEMISTRY
Sb 3.9 2.5
As 3.2 3.4
Cd 1 2.51 l< 2.3]
Cu+Pb+Zn 2.5 3.1
Hg 1.5 < 2.4
Ni 0.7 0.7
Phenol | 2.6| < 5.9
Pentachlorophenol U 2.0 < 3.0
LPAH < 6.3 <26.
HPAH < 3.7 <35.
Chlor. benzenes U 1.4 < 2.7
Chlor. butadienes < 1.4 |< 3.7|
Phthalates l< 5.8| < 1.4
PCBs 1.3 |< 5. 6l
4-Methyl phenol g.Q <17.
Benzyl alcohol 6.1 < 2.2
Benzole acid < 0.3 < 1.4
Dibenzofuran | 5.2) I 26. I
n-Nitrosodiphenylamine U 1.2 < 1.0
Tetrachloroethene --- —
SEDIMENT TOXICITY
Amphipod bioassay — 1.7
Oyster bioassay --- 1.6
INFAUNAC
Total benthos --- 1.0
Polychaetes --- 1.0
Molluscs --- 1.0
Crustaceans — 1.0
E L E
BL-S2
5.1
8.9
2.2
5.6
4.6
0.7
< 5.0
< 2.4
<32.
<45.
< 6.8
< 2.4
< 2.8
j< 6.6|
14.
< 2.3
< 5.7
28.
< 4.0
U 1.0
2.1
1.6
1.0
1.0
1.0
1.0
V A T I 0 N S3
BL-S1
4.1
| 11. |
2.0
5.6
3.6
0.8
|< 4.4|
< 1.1
<23.
<45.
< 1.8
U 1.7
< 3.7
< 6.6
< 9.0
< 2.0
< 0.7
1 19- 1
< 1.4
U 0.5
1.9
1.4
1.0
1.0
1.0
1.0
REFERENCE
VALUE b
110. ppb
3370. ppb
950. ppb
35000. ppb
40. ppb
1740. ppb
< 33. ppb
U 33. ppb
< 41. ppb
< 79. ppb
U 21. Ppb
U 62 . ppb
< 280. ppb
U 6. ppb
< 13. ppb
U 10. ppb
< 140. ppb
U 3.7 ppb
U 4.1 ppb
U 10. ppb
9.3 %
13.0 %
d
d
d
d
a See Table 6.1 for footnotes.
6.6
-------
TABLE 6.4. ACTION ASSESSMENT MATRIX OF SEDIMENT CONTAMINATION, SEDIMENT TOXICITY,
AND BIOLOGICAL EFFECTS INDICES FOR COMMENCEMENT BAY STUDY AREAS
CITY S E G M E
VARIABLE CI-S3
SEDIMENT CHEMISTRY
Sb 4.9
As 5.6
Cd 3.8
Cu+Pb+Zn 10.
Hg 6.1
Ni 0.9
Phenol 11.
Pentachlorophenol < 1.8
LPAH <120.
HPAH 130.
Chlor. benzenes < 3.6
Chlor. butadienes | < 2.4|
Phthalates < 2.7
PCBs [ < 7.9|
4-Methyl phenol IQ_
Benzyl alcohol 3.0
Benzole acid < 1.5
Dibenzofuran | 52. |
n-Nitrosodiphenylamine U 1.5
Tetrachloroethene —
SEDIMENT TOXICITY
Amphipod bioassay 2.6
Oyster bioassay 2.0
INFAUNA °
Total benthos 1.0
Polychaetes 1.1
Molluscs 1.0
Crustaceans 0.5
N T
CI-S2
5.4
6.8
6.5
28.
6.8
1.5
<10.
2.1
<110.
160.
27.
< 0.8
< 9.2
20.
45.
U 1.0
< 0.2
72.
32.
U 1.0
1.5
1 23"
6.8
4.6
24.2
6.1
E L
EVA
CI-S1
loT"
4.9
2.5
26.
3.1
0.7
8.7
< 1.9
<120.
140.
< 7.5
< 2.0
< 9.
12.
<41.
6.2
< 1.8
58.
<15.
U 1.0
3.2
3.0
0.5
0.5
7.7
2.5
T I 0 N S3
REFERENCE
VALUE b
110. ppb
3370. ppb
950. ppb
35000. ppb
40. ppb
1740. ppb
< 33. ppb
U 33. ppb
< 41. ppb
< 79. ppb
U 21. ppb
U 62 . ppb
< 280. ppb
< 6. ppb
< 13 ppb
U 10. ppb
< 140. ppb
U 3.7 ppb
U 4.1 ppb
U 10. ppb
9.3 %
13.0 %
d
d
d
d
See Table 6.1 for footnotes.
6.7
-------
TABLE 6.5 ACTION ASSESSMENT MATRIX OF SEDIMENT CONTAMINATION, SEDIMENT TOXICITY,
AND BIOLOGICAL EFFECTS INDICES FOR COMMENCEMENT BAY STUDY AREAS
RUSTON SEGMENT ELEVATIONS3
VARIABLE RS-S3 RS-S2 RS-S1
SEDIMENT CHEMISTRY
Sb 140.
As 120.
Cd 6.2
Cu+Pb+Zn 42.
Hg 6.9
Ni 1.1
1100.
1400.
58.
260.
370.
4.9
8.6
1 5.7 I
1.8
I 6.1 1
5.8
1.2
Phenol 1.4 | TF] | 4.5]
Pentachlorophenol U 1.1 < 1.1 < 0.9
LPAH < 3.5
HPAH 6.4
<150.
130.
<51.
<68.
Chi or. benzenes U1.4 <4.1 <3.0
Chlor. butadienes < 1.5
Phthalates < 2.4
PCBs < 1.9
4-Methyl phenol y 0.8
Benzyl alcohol U 1.0
< 2.1
< 6.9
41.
< 7.8
< 1.2
< 1.3
< 3.0
< 2.4
<16.
< 1.8
Benzole acid U 0.2 < 0.8 < 0.2
Dibenzofuran < 3.0
n-Nitrosodiphenylamine < 5.5
<160.
<22.
|<36. |
U 0.9
Tetrachloroethene — — —
SEDIMENT TOXICITY
Amphipod bioassay 2.0 | 6.5| 2.5
Oyster bioassay 1.1 3.2 | 1 . 8 |
c
INFAUNA
Total benthos --- | 2. 2 1 0.4
Polychaetes — 1.6 0.3
Molluscs --- | 14.6| 0.6
Crustaceans --- 2.0 0.4
REFERENCE
VALUE b
110. ppb
3370. ppb
950. ppb
35000. ppb
40. ppb
1740. ppb
< 33. ppb
U 33. ppb
< 41. ppb
< 79. ppb
U 21. ppb
U 62. ppb
< 280. ppb
U 6. ppb
< 13. ppb
U 10. ppb
< 140. ppb
U 3.7 ppb
U 4.1 ppb
U 10. ppb
9.3 %
13.0 %
d
d
d
d
a See Table 6.1
for footnotes.
6.8
-------
TABLE 6.6. MEAN REFERENCE VALUES USED TO CALCULATE
ELEVATIONS ABOVE REFERENCE FOR BENTHIC INFAUNA
Reference
Group3
A
B
C
D
E
F
Stations
Included
BL-11, BL-21
BL-31
BL-13
CR-ll.CR-12
CR-13,CR-14
BL-28, BL-11
BL-21, BL-31
BL-28, BL-11
BL-21, BL-31
CR-ll.CR-12
CR-13.CR-14
BL-11, BL-21
BL-31, BL-13
Percent
Finesb
55-64
84
4-21
37-64
4-84
55-84
Mean
Total
10,983
10,604
3,683
9,013
9,331
10,889
Benthic Invertebrate Abundance/m2
Polychaetes
4,254
4,400
1,644
3,452
3,642
4,291
Molluscs
6,049
5,933
1,016
4,980
5,171
6,020
Crustaceans
635
217
934
529
467
530
a Different groupings of the reference stations in Table 3.24 were formed
to represent the different benthic habitats included in Commencement Bay
study areas and segments.
b The range of percent fine-grained material (i.e., silt and clay) present
in sediments sampled at the reference stations.
6.9
-------
TABLE 6.7. IDENTIFICATION OF REFERENCE GROUPS USED TO CALCULATE BENTHIC
ABUNDANCE ELEVATIONS ABOVE REFERENCE FOR STUDY AREAS AND SEGMENTS
Study Area/ Percent Fine-Grained
Segment3 Material** Reference Group0
Hylebos 6-86 E
Sitcum 76-81 F
Milwaukee 85-89 B
St. Paul 26-67 D
Middle 56 A
City 28-80 D
Ruston-Pt. Defiance 3-33 C
HYS1
HYS2
HYS3
HYS4
HYS5
HYS6
CIS1
CIS2
CIS3
RSS1
RSS2
48 - 79
76 - 86
61
61
6 - 78
86
39 - 78
74
28 - 80
13 - 29
3 - 33
D
F
A
A
D
B
D
A
D
C
C
a Blair Waterway and Segments BLS1, BLS2, and BLS3 are not listed because
their component stations (except BL-25) were considered representative
of reference conditions. No benthic data were collected for BLS4 or RSS3
b The range of percent fine-grained material (i.e., silt and clay) present
in sediments sampled in each study area or segment.
c Reference groups are defined in Table 6.6.
6.10
-------
high values for selected chemicals in Segment HYS5 near the mouth of the
waterway.
Relatively lower levels of chemical contamination were observed in
the adjacent Blair Waterway. These lower contaminant levels corresponded
to a lack of significant toxicity or benthic effects indicators when averaged
over any segment (Table 6.3). Within City Waterway (Table 6.4), contamina-
tion, toxicity, and benthic effects were highest near the head and within
the Wheeler-Osgood branch of the waterway. The mouth of City Waterway
was comparable in number and magnitude of significant indicators with Segment
RSS1 along the eastern Ruston-Pt. Defiance Shoreline (Table 6.5). The
extreme metals contamination and high level of organic compound contamination
within Segment RSS2 corresponded with the largest number and highest average
magnitude of toxicity and benthic effects indicators along the Ruston-
Pt. Defiance Shoreline.
6.2.2 Application of Action Levels to Determine Problem Areas
Action-level guidelines are summarized in Table 6.8. A problem area
requiring further evaluation is identified when values for three or more
indices are significantly elevated. Using this guideline, problem areas
were indicated within all Commencement Bay study areas and segments shown
in Tables 6.1-6.5. Several of the segments within the larger study areas
met this criterion only when study area-wide values for English sole pathology
and bioaccumulation were considered. According to Table 6.8 guidelines,
significant bioaccumulation of PCBs in Hylebos, Blair, Sitcum, and City
Waterways may warrant source identification based solely on the prediction
of possible significant health effects.
Six segments within the larger study areas had significant EAR_for
all three of the site-specific indicators (contamination, sediment toxicity,
and benthic effects) including:
§ Segments HYS1, HYS2, and HYS5 in Hylebos Waterway
• Segments CIS1 and CIS2 in City Waterway
• Segment RSS2 along the Ruston-Pt. Defiance Shoreline.
A problem area was also indicated in Segment HYS4 of Hylebos Waterway
based on mollusc abundances being depressed by greater than 95 percent
relative to reference conditions (i.e., EAR >20). According to guidelines
in Table 6.8, this condition indicated a problem area regardless of the
values for other indicators.
6.2.3 Ranking of Study Areas and Segments
As discussed, average conditions in all study areas and segments exceeded
the thresholds required for further definition of problem areas for source
evaluation. Criteria presented in Table 6.9 were applied to action assessment
matrices (Tables 6.1-6.5) to rank study areas and segments. These rankings
were based on average conditions in each area, and provide an overview
of the relative contamination and contaminant effects throughout Commencement
Bay. This relative ranking process was independent from the action guidelines
6.11
-------
TABLE 6.8. ACTION-LEVEL GUIDELINES
Condition Observed
Threshold Required for Action
I. Any THREE OR MORE significantly
elevated indices9
II. TWO significantly elevated
indices
1. Sediments contaminated, but
below 80th percentile PLUS:
Bioaccumulation without an
increased human health risk
relative to that at the
reference area, OR
Sediment toxicity with less
than 50 percent mortality
or abnormality, OR
Major benthic invertebrate
taxon depressed, but by less
than 95 percent.
2. Sediments contaminated but
below 80th percentile PLUS
elevated fish pathology
Any TWO significantly ele-
vated indices, but NO ele-
vated sediment contamina-
tion
Threshold exceeded, continue with
definition of problem area
No immediate action. Recommend
site for future monitoring.
Threshold for problem area definition
exceeded if elevated contaminants
are considered to be biologically
available. If not, recommend site
for future monitoring.
Conduct analysis of chemistry to
distinguish site from adjacent
areas. If test fails, no immediate
action warranted. Otherwise, threshold
exceeded for characterization of
problem area. Re-evaluate signifi-
cance of chemical indicators.
III. SINGLE significantly elevated
index
1. Sediment contamination
If magnitude of contamination exceeds
the 80th percentile for all study
areas, recommend area for potential
source evaluation at a low priority
relative to areas exhibiting contam-
ination and effects.
6.12
-------
TABLE 6.8. (Continued)
2. Bioaccumulation
3. Sediment toxicity
4. Depressed benthic abundance
5. Fish pathology
Increased human health threat,
defined as: Prediction of >_ 1
additional cancer cases in the
exposed population for significantly
elevated carcinogens, OR
For noncarcinogens, exceedance
of the acceptable daily intake
value is required.
Greater than 50 percent response
(mortality or abnormality).
95 percent depression or greater
of a major taxon (equals an EAR
of 20 or greater).
Insufficient as a single indicator.
Reconmend site for future monitoring.
Check adjacent areas for significant
contamination, toxicity, or biological
effects.
a Combinations of significant indices are from independent data types (i.e.
sediment chemistry, bioaccumulation, sediment toxicity, benthic infauna,
fish pathology).
Significant indices are defined as follows:
Sediment chemistry = chemical concentration at study site exceeds highest
value observed at any Puget Sound reference area.
Sediment toxicity, benthic abundance, bioaccumulation, and pathology =
statistically significant (P <0.05) difference between study area and reference
area.
6.13
-------
TABLE 6.9. SUMMARY OF RANKING CRITERIA FOR SEDIMENT CONTAMINATION,
TOXICITY, AND BIOLOGICAL EFFECTS INDICATORS
Indicator
Criteria
Score
Total Metals
Contamination
ficant
Total Organic Compound
Contamination
Toxicitya
Macroinvertebrates
(Abundance)b
Bioaccumulation
(Fish Muscle)
Fish Pathology
(Liver Lesions)^
Concentration not signi
Significant; EAR <10
Significant; EAR 10-<50
Significant; EAR 50-<100
Significant; EAR >100
Concentration not significant
Significant; EAR <10
Significant; EAR 10-<100
Significant; EAR 100-<1000
Significant; EAR >1000
No significant bioassay response
Amphipod OR oyster bioassay significant
Amphipod AND oyster bioassays significant
>50 percent response in EITHER bioassay
No significant depressions
1 significant depression
2 significant depressions
>. 3 significant depressions
>. 1 taxon with >_ 95% depression
No significant chemicals
1 significant chemical
2 significant chemicals
2. 3 significant chemicals
Significant bioaccumulation of >_ 1 chemical
posing a human health threat0
No significant lesion types
1 significant lesion type
2 significant lesion types
2. 3 significant lesion types
2. 5% prevalence of hepatic neoplasms
Maximum Possible Score
0
1
2
3
4
0
1
2
3
4
0
2
3
4
0
1
2
3
4
0
1
2
3
0
1
2
3
4
24
a Toxicity based on amphipod mortality and oyster larvae abnormality bioassays.
b Taxa considered were total benthic taxa, Polychaeta, Mollusca, and Crustacea.
*• As defined in Table 6.8: Action-Level Guidelines.
" Lesions considered were hepatic neoplasms, preneoplastic nodules, megalocytic
hepatosis, and nuclear pleomorphisms.
6.14
-------
used to define problem areas. A separate ranking of defined problem areas
within each study area is presented in Section 6.4. That ranking is based
on the maximum contamination and effects observed in each problem area.
Results of the ranking of study areas and segments for chemical contamina-
tion are given in Table 6.10. Scores noted in Table 6.9 were based solely
on the magnitude of chemical contamination. The scale used for metals
differed from that for organic compounds to provide better resolution of
the typically smaller range in metals concentrations among waterways compared
with that of organic compounds. Separate rankings are given in Table 6.10
based on the average EAR of metals, organic compounds, and the sum of metals
and organic compounds. When study areas or segments had the same score
for the magnitude of chemical contamination, the areas were further prioritized
by the number of chemicals with significant EAR. For example, the average
metals contamination in sediments from Hylebos, Middle, City, and Sitcum
Waterways was of the same order of magnitude (i.e., EAR 10-<50) resulting
in a score of 2 for each waterway. Of these waterways, Hylebos Waterway
had the largest number of metals or groups of metals (5) with significant
EAR and Sitcum Waterway had the least (3). Although Middle and City Waterways
had the same score for metals contamination and the same number of metals
with significant EAR (4), Middle Waterway was ranked higher because the
absolute magnitude of contamination in Middle Waterway was higher than
that in City Waterway. This sequential evaluation of chemical contamination
was used to rank all study areas and segments relative to each other.
Segment RSS2 along the Ruston-Pt. Defiance Shoreline had the highest overall
level of contamination, while Blair Waterway, Milwaukee Waterway, and the
eastern shoreline of the Ruston-Pt. Defiance Shoreline had the lowest overall
levels of contamination.
A separate ranking of study areas and segments by the average number
and magnitude of statistically significant (P<0.05) sediment toxicity and
biological effects is given in Table 6.11. For toxicity and biological
effects indices, areas were scored primarily by the number of significant
indicators. As shown in Table 6.9, the highest score of 4 in the toxicity
and biological effects indices was assigned for special concerns related
to the severity of the toxic response or biological effect. No attempt
was made to resolve tied scores among segments in Table 6.11 as was done
for chemical contamination ranked in Table 6.10. Based on this scoring,
Sitcum Waterway was ranked highest of all study areas, primarily because
PCB bioaccumulation posed potential health concerns and hepatic neoplasms
exceeded 5 percent prevalence. Sitcum Segment SIS1 and Hylebos Segment
HYS2 ranked the highest for toxicity and biolgical effects on a segment
basis. Average conditions along the Ruston-Pt. Defiance Shoreline ranked
lowest among study areas, and Segments RSS1 and RSS3 ranked lowest among
segments. When contributions from fish pathology and bioaccumulation indices
were removed, Hylebos and City Waterways ranked the highest among study
areas and also contained the highest ranked segments for combined toxicity
and benthic effects.
Scores for study area segments based on the maximum observed values
at any station within the segment for contamination, sediment toxicity,
and benthic effects indices are listed in Table 6.12. Maximum observed
conditions within each segment were used for scoring the site-specific
indices so that worst-case conditions of problem areas within each segment
6.15
-------
TABLE 6.10. RANKING OF STUDY AREAS AND SEGMENTS BY AVERAGE MAGNITUDE
AND NUMBER OF SIGNIFICANT SEDIMENT CONTAMINANTS
Total Metals3
Total Organic Compounds3
Total Chemicals3
Area Number of
or Significant
Segment Metals Score
Ruston
Hylebos
Middle
City
Sitcum
5
4
4
3
Blair 1
Milwaukee 1
2
2
2
2
1
1
Area Number of
or Significant
Segment Compounds Score
St. Paul
0
St. Paul
Hylebos
City
Middle
Ruston
Blair
Sitcum
Milwaukee
13
12
10
10
11
10
7
3
3
3
3
Area Number of
or Significant
Segment Chemicals Score
Ruston
16
Hylebos
City
Middle
Sitcum
St. Paul
Blair
Milwaukee
18
16
14
13
7
12
8
5
5
5
4
4
3
3
RSS2
RSS3
HYS1
MDS1
CIS2
HYS2
SIS1
CIS1
HYS3
HYS5
BLS1
HYS4
CIS3
HYS6
BLS2
RSS1
MIS1
BLS4
BLS3
SPS1
6
5
5
4
4
4
3
3
3
3
1
3
3
2
2
2
1
1
1
0
4
4
2
2
2
2
2
2
2
2
2
1
1
1
1
1
1
1
1
0
SPS1
CIS1
HYS2
HYS5
HYS4
HYS1
RSS2
CIS2
MDS1
CIS3
BLS2
SIS1
HYS3
HYS6
BLS3
BLS1
MIS1
RSS1
BLS4
RSS3
7
12
11
11
11
10
10
10
10
9
12
10
10
10
9
8
7
6
5
2
4
3
3
3
3
3
3
3
3
3
2
2
2
2
2
2
2
2
1
1
RSS2
HYS1
HYS2
CIS1
CIS2
MDS1
HYS5
RSS3
HYS4
SIS1
HYS3
CIS3
BLS1
SPS1
BLS2
HYS6
BLS3
MIS1
RSS1
BLS4
16
15
15
15
14
14
14
7
14
13
13
12
9
7
14
12
10
8
8
6
7
5
5
5
5
5
5
5
4
4
4
4
4
4
3
3
3
3
3
2
3 Number of significant chemicals (metals or organic compounds)
and groups of chemicals listed in the action assessment matrices
Total chemicals are the sum of metals and organic compound scores.
in Table 6.9.
includes individual
(Tables 6.1-6.5).
Scores are defined
6.16
-------
TABLE 6.11. RANKING OF STUDY AREAS AND SEGMENTS BY THE AVERAGE MAGNITUDE
OF SEDIMENT TOXICITY AND BIOLOGICAL EFFECTS
Scored
Area
or Sediment Macro- Muscle Liver
Segment Toxicity invertebrates Bioaccumulation Pathology
Sitcum
Hylebos
City
Blair
Middle
Milwaukee
St. Paul
Ruston
HYS2
SIS1
CIS2
HYS4
HYS5
HYS1
CIS1
HYS6
CIS3
RSS2
MDS1
HYS3
MIS1
BLS1
BLS2
BLS3
SPS1
BLS4
RSS1
RSS3
2
3
3
2
0
2
2
2
3
2
2
0
3
2
2
2
3
4
0
0
2
0
0
0
2
-b
2
0
1
1
1
0
2
0
1
0
3
1
4
4
1
1
2
0
0
2
2
0
0
0
0
0
1
_-b
0
-b
4
4
4
4
0
2
1
1
4
4
4
4
4
4
4
4
4
1
0
4
2
4
4
4
1
4
1
1
4
1
0
1
4
1
0
0
1
4
0
1
1
1
0
1
0
0
4
1
1
1
1
1
0
0
0
0
Total
11
9
8
7
6
5
4
3
11
11
10
9
9
8
8
7
7
7
6
5
5
5
5
5
4
4
3
1
Scores are defined
No data available.
in Table 6.9.
6.17
-------
TABLE 6.12. RANKING OF STUDY AREA SEGMENTS BY MAXIMUM OBSERVED
SEDIMENT CONTAMINATION, TOXICITY, AND BIOLOGICAL EFFECTS
Maximum Chemical
Segment
HYS1
HYS2
HYS3
HYS4
HYS5
HYS6
BLS1
BLS2
BLS3
BLS4
SIS1
MIS1
SPS1
MDS1
CIS1
CIS2
CIS3
RSS1
RSS2
RSS3
Metals
2
2
2
2
2
2
2
2
1
1
2
1
2
3
3
2
2
2
4
4
Organic
Compounds
3
3
3
2
4
2
3
3
2
2
3
3
4
3
3
3
2
3
3
2
Score3
Total
5
5
5
4
6
4
5
5
3
3
5
4
6
6
6
5
4
5
7
6
Bioassay
2
3
0
0
2
0
0
2
0
— b
2
2
4
0
4
2
3
3
4
2
Maximum
Benthos
4
4
0
4
1
0
0
0
0
_.b
1
0
4
Od
4
4
0
0
4
— b
Toxicity/Effects Score3
Muscle
Bioaccum
4
4
4
4
4
4
4
4
4
4
4
2
1
0
4
4
4
1
1
1
Liver
Pathology
1
1
1
1
1
1
1
1
1
1
4
1
0
4
0
2
0
0
0
0
Total
11
12
5
9
8
5
5
7
5
5
11
5
9
4
12
12
7
4
9
3
TOTAL
SCORE3
16
17
10
13
14
9
10
12
8
8C
16
9
15
10
18
17
11
9
16
9
3 Segments defined for data analysis were scored by the maximum observed level of contamina-
tion, toxicity, or benthic effects at any station within the segment. Bioaccumulatioi
and pathology scores reflect average waterway conditions only. Scores are defined ii
Table 6.9.
b No data available.
c Based on partial set of toxicity/effects indicators
d Benthic depressions were significant (rank=2) for Station MD-12 in Middle Waterwa;
when tested among waterways, but not among all stations because of the effect of multipli
comparisons on the critical t-value for the respective significance tests (i.e., waterwa,
versus station level).
6.18
-------
were considered. Scores for fish liver pathology and muscle bioaccumula-
tion in Table 6.12 still reflect the average conditions observed throughout
each study area. Scores for all five indicators are summed in Table 6.12
by segment to combine information for all available indicators. Segments
are listed in Table 6.12 in geographic order rather than rank order to
facilitate comparisons of conditions within a study area and between adjacent
study areas.
After segments were prioritized according to average conditions (Tables
6.10, 6.11) and worst-case conditions (Table 6.12), results of the two
methods were compared (Figure 6.2). Selected segments in Hylebos, Sitcum,
and City Waterways and Segment RSS2 along the Ruston-Pt. Defiance Shoreline
scored high by both methods. Milwaukee Waterway (MIS1), Blair Waterway
segments, and Segment RSS1 on the eastern Ruston-Pt. Defiance Shoreline
scored low by both methods.
6.3 SPATIAL EXTENT AND RANKING OF PROBLEM AREAS
Although chemical contamination data are available for all sediment
samples collected, toxicity and macroinvertebrate abundance data are available
only for some of the samples. The chemical data set is therefore the most
useful for defining the spatial extent of problem areas, and was used to
delineate the areas indicated in Table 6.13. All available data were used,
including predictions of problem sediments based on sediment chemistry
at non-biological stations and quantitative relationships (Section 4) that
defined apparent effect thresholds for chemicals. Segments containing
each problem area were ranked according to the "maximum" score for worst-
case conditions in the segment (Table 6.13). The top eight problem areas
all exhibited significant contamination, sediment toxicity, and benthic
effects, in addition to having at least one significant indicator of fish
pathology or bioaccumulation. The lowest ranking problem areas were contained
in segments that did not exhibit significant sediment toxicity or benthic
effects. Based solely on quantitative relationships, significant toxicity
or benthic infaunal effects would be predicted at the stations indicated
in Table 6.13 if biological data were collected.
The spatial extent and general priority for source evaluation of all
problem areas identified in Commencement Bay are summarized in Figure 6.3.
Problem areas defined only by mid-channel stations in the current study
were assumed to extend from shoreline to shoreline, unless historical data
indicated otherwise (e.g., nearshore historical samples were uncontaminated).
At the highest priority sites, at least four indicators were significant,
including all three site-specific indicators. Eight problem areas received
highest priority for source evaluation, including three within Hylebos
Waterway, two within City Waterway, and one within each of Sitcum and St. Paul
Waterways and along the Ruston-Pt. Defiance Shoreline. The second priority
sites are "hot spots" where chemical contamination exceeded an "apparent
effect threshold" (AET), and both bioassays were significant or multiple
benthic depressions were observed within the problem area. Four problem
areas received second priority for source evaluation, including one each
within Hylebos, Middle, and City Waterways, and at Station RS-13 along
the eastern Ruston-Pt. Defiance Shoreline.
6.19
-------
SCORE"
SEGMENT
RE'
14
13
12
11
10
9
8
7
6
y f f * f ;
^ •> > '
•
' , ,
^ ' , *
\
', ,
%
v.v ^ ,
'<*/£•( ^ ~> •, •. .
SEGMENT
HYS2
SIS1, CIS2
HYS5, RSS2
HYS4, CIS1, HYS1
SPS1
MDS1, CIS3
HYS6
HYS3, BLS1, RSS3
BLS2, BLS3
Ml^l
RSS1 Rl S4
AVERAGE
RANK
METHOD
17
16
15
14
13
12
11
10
9
-^
CIS1
HYS2, CIS2
RSS2, SIS1, HYS1
SPS1
HYS4
BLS2
BLS1
RSS3, RSS1, MIS1, HYS6
BLS2, BLS4
MAXIMUM
RANK
METHOD
•SCORES ARE SUMS FOR CHEMICAL AND BIOLOGICAL INDICATORS
FROM TABLES 6.10 AND 6.11
"SCORES ARE SUMMARIZED IN TABLE 6.12
Figure 6.2. Relative ranking of study area segments by average
and maximum observed contamination, toxicity, and
biological effects.
6.20
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TABLE 6.13. DEFINITION AND RELATIVE RANKING OF PROBLEM AREAS
Total
Segment Contaminant-
Containing Toxcity-Effects
Problem Areaa Scoreb Stations Included in Problem Areac
CIS1
HYS2
CIS2
RSS2
SIS1
HYS1
SPS1
HYS5
HYS4
BLS2
CIS3
MDSie
HYS3e
BLSie
RSS3
RSS1
MISie
HYS66
BLS36
BLS46
18
17
17
16
16
16
15
14
13
12
11
10
10
10
9
9
9
9
8
8
CI-ll,CI-12,CI-13,CI-14,CI-15,CI-18d
HY-20,HY-21,HY-22,HY-23
CI-02,CI-16
RS-03,RS-16,RS-17,RS-18,RS-19,RS-20,RS-21
SI-11,SI-12,SI-13,SI-14,SI-15
HY-11,HY-12,HY-13,HY-14,HY-15,HY-16,HY-17,
HY-18.HY-19
SP-13,SP-14,SP-15,SP-16
HY-03,HY-36,HY-38,HY-39,HY-40,HY-41,HY-42,
HY-45,HY-46,HY-47
HY-32.HY-33
BL-04,BL-16,BL-18,BL-19,BL-20,BL-23,BL-26,B-15
CI-20,CI-21
MD-11,MD-13
HY-27,HY-31
BL-01,BL-14
RS-22,RS-24
RS-13
RS15f
-none-
CB-11
BL-27,BL-29,BL-30
CB-12
a Problem areas encompass all stations sampled in 1984 only in Segments HYS1,
SIS1, CIS2, RSS2, RSS3, and possibly MDS1 (Station MD-12 in this segment was
close to the AET for several chemicals).
b Total scores using the maximum rank method are summarized in Table 6.12.
Segments are listed by decreasing magnitude of these scores.
c Stations shown have sediment concentrations (by various normalizations) of
some chemical above its AET defined in Section 4. Biological data were not
available for all stations listed.
d Station CI-18 may not be contained in the same problem area defined for the
remainder of the Segment CIS1 stations listed.
6.21
-------
TABLE 6.13 (Continued)
e No stations with biological data in these segments had sediment chemical
concentrations exceeding their AET.
f This station had significant organic and metals contamination only when normalized
to percent fine-grained material. There were no biological data available so
no total toxicity-effects score has been determined. Station RS-15 is considered
a separate potential problem area in Segment RSS1 from that defined by Station
RS-13.
6.22
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COMMENCEMENT
BAY
HIGHEST PRIORITY PROBLEM AREAS
SECOND PRIORITY PROBLEM AREAS
POTENTIAL PROBLEM AREAS
(NO CONFIRMING BIOLOGICAL
DATA AVAILABLE)
POTENTIAL PROBLEM AREA BY
HISTORICAL DATA ONLY
CHEMICALS EXCEED APPARENT
EFFECTS THRESHOLD
CHEMICALS BELOW APPARENT
EFFECTS THRESHOLD
ro
co
CITY
WATERWAY
Figure 6.3.
Definition and prioritization of Commencement
Bay problem areas.
-------
RUSTON
no
N
o
I
r
o
COMMENCEMENT
BAY
4000
J I FEET
TACOMA
1
METERS
1000
HIGHEST PRIORITY PROBLEM AREAS
SECOND PRIORITY PROBLEM AREAS
POTENTIAL PROBLEM AREAS
(NO CONFIRMING BIOLOGICAL
DATA AVAILABLE)
POTENTIAL PROBLEM AREA BY
HISTORICAL DATA ONLY
CHEMICALS EXCEED APPARENT
EFFECTS THRESHOLD
CHEMICALS BELOW APPARENT
EFFECTS THRESHOLD
Figure 6.3. (Continued),
-------
Third priority sites included those where chemical contamination exceeded
an AET, and one of the bioassays was significant or a single benthic taxon
was significantly depressed in the problem area. Two problem areas received
third priority for source evaluation, including one within each of Segment
BLS2 in Blair Waterway and Segment RSS3 along the Ruston-Pt. Defiance Shoreline.
Significant amphipod bioassay responses were observed at two stations in
Milwaukee Waterway but no chemicals were found above their AET. As discussed
in Section 4, these amphipod responses may have resulted from effects of
grain size. The lowest priority sites for source evaluation included those
where no sediment toxicity or benthic effects were observed, but where
additional chemical data suggested that toxicity or benthic effects may
have occurred at non-biological stations. The remaining six areas in Table 6.13
fell into this priority category, including two potential problem areas
within Hylebos Waterway, three areas within Blair Waterway, and second
potential problem area within Segment RSS1 on the eastern Ruston-Pt. Defiance
Shoreline (Station RS-15). This latter area did not exhibit highly elevated
concentrations of contaminants on a dry-weight basis, but AET were exceeded
after the data were normalized to percent fine-grained material or organic
carbon content.
Problem area boundaries shown in Figure 6.3 were extended, as appropriate,
where historical data suggested that a problem existed. According to action-
level guidelines in Table 6.8, amphipod toxicity data from Swartz et al. (1982)
showing >50 percent response would identify historical problem sediments.
Historical chemical concentrations that exceeded an AET were also considered
appropriate for defining problem area boundaries. In general, these historical
toxicity and chemical data reinforced current observations. The problem
area in Segment HYS2 was expanded slightly as result of these comparisons,
and historical high toxicity (>50 percent mortality) in the upper turning
basin of Segment HYS1 reinforced a decision to extend the problem area
to include the entire segment. High toxicity also was reported at the
head of Milwaukee Waterway, at the Lincoln Avenue Drain on the north side
of Blair Waterway, and at a drain near the head of St. Paul Waterway.
Present data for sediments near these locations did not indicate a problem.
Source evaluations are recommended for at least the 14 problem areas
in priority categories 1, 2, and 3 discussed in this section.
6.4 CHEMICAL CHARACTERIZATION OF PROBLEM AREAS
This section summarizes chemical characteristics of the 14 problem
areas reconmended for source evaluation (Section 6.4). Chemical characteristics
of the remaining problem areas also are summarized briefly. This analysis
was conducted 1) to identify chemicals present at high concentrations within
each problem area and 2) to identify chemicals that appear either to distinguish
problem areas from one another or to establish apparent relationships among
them. In Section 6.5, quantitative relationships among contaminants, sediment
toxicity, and biological effects are used to prioritize potential problem
chemicals in each problem area.
To provide a reasonably consistent data set for comparing the chemistry
of problem areas, the analysis is based primarily upon data from the March, 1984
sediment survey. These data were collected synoptically using similar
procedures, and were analyzed by the same laboratory, therefore, they should
6.25
-------
have the lowest intra-sample variance due to other factors besides field
variability. Distributions of the measured chemicals also reflect those
of unmeasured chemicals from similar sources and results must be interpreted
within this context.
6.4.1 Hylebos Waterway
Two high priority problem areas were identified within Segments HYS1
and HYS2 of upper Hylebos Waterway. The entire reach of upper Hylebos
Waterway was highly contaminated with HPAH and most of the metals, although
the concentrations of only some metals exceeded toxicity or benthic effects
AET. Distributions of these chemicals were not clearly separated between
the two segments. Both groups of substances (especially HPAH) exhibited
high EAR near two sites, one along the south side of the channel at Stations
HY-15 and HY-16, and a second on the south side at Station HY-22. Compositional
differences in the HPAH and LPAH between these two sites indicated that
the PAH did not necessarily originate from the same source. Compositional
similarities were generally too weak to establish a clear relationship
between the HPAH at the sites, supporting the definition of two problem
areas. Metals in the sediments of upper Hylebos Waterway exhibited a general
spatial distribution similar to that of the PAH. Arsenic and copper were
present at relatively high levels compared to those of the other metals,
but only arsenic was present at concentrations above toxicity or benthic
effects AET. Although this composition was not observed at most stations
in Commencement Bay, it was characteristic of some sediments along the
Ruston-Pt. Defiance Shoreline, as discussed in Section 6.4.8. PCB and
chlorobenzene concentrations were elevated above AET only in the Segment
HYS2 problem area, distinguishing this problem area from that in Segment
HYS1. Sediments from Station HY-27 in Segment HYS3 also contained high
PCB concentrations that exceeded toxicity AET. There was no evidence that
the problem area in Segment HYS2 extended to include the "hot spot" in
Segment HYS3.
A "hot spot" problem area was identified in Segment HYS4 of Hylebos
Waterway, east of the llth Street Bridge (Stations HY-32 and HY-33). This
segment included a long reach of waterway with few sampling stations.
Concentrations of metals and chlorinated compounds in this area increased
toward adjacent segments, indicating that advective transport from outside
of the segment may have contributed many of these substances. The PAH,
however, exhibited high EAR at Station HY-33, and decreased in concentration
with distance from this station. HPAH at Station HY-33 were unique because
of the high EAR for benzo(a)pyrene compared to those of other HPAH. Finally,
4-methylphenol was present at Station HY-33 at the highest EAR observed
for that compound in Hylebos Waterway. This concentration did not exceed
either the toxicity or benthic effects AET. Sediment concentrations appeared
to show a decreasing gradient with distance from Station HY-33. While
sediment from this problem area generally did not contain chemicals with
high EAR, gradients for the PAH and 4-methylphenol indicated presence of
a nearby source. The limits of the "hot spot" were poorly defined, but
could have extended from approximately the llth Street Bridge east to Station
HY-32.
A high priority problem area was identified in Segment HYS5, west
of the llth Street Bridge. While cross-channel sampling was limited, sediments
6.26
-------
from the southern side of the waterway appeared to be more contaminated
than those from the middle or north side. A single sample from the large
shallow area on the north shore (HY-02) indicated that this area was uncontami-
nated (i.e., no concentrations exceeded the range of concentrations observed
in any Puget Sound reference area). Anomalously low EAR for all chemicals
were measured at Station HY-44. The simplest explanation is that this
station contained relict sediments either dumped at the site in a dredging
operation or exposed by ship scour. Concentrations of the majority of
the chemicals measured in sediments along the south shore were not greatly
elevated above reference conditions, although selected chlorinated compounds
were present in the highest concentrations observed throughout Commencement
Bay. Their spatial distributions were not as simple as might have been
expected if all compounds had originated from a single source. Intertidal
and shallow subtidal sediments along the southern shore about 3,000 feet
from the waterway mouth were highly contaminated with chlorinated ethenes.
The concentrations of these compounds sometimes eceeded toxicity and benthic
effects AET by several orders of magnitude. These very high contaminant
levels were restricted to the nearshore area, and declined rapidly with
distance offshore and alongshore. Chlorinated butadiene concentrations
exhibited the strongest single gradient, maximizing at Stations HY-43,
HY-46, and HY-47 (all contiguous nearshore stations on the south side of
the channel). Only concentrations of HCBD exceeded AET in this area.
Concentrations of a tentatively identified pentachlorocycolpentane isomer
and many of the chlorinated benzenes were elevated above AET at Station
HY-46 and also at Station HY-36, near the llth Street Bridge. PAH concen-
trations were also elevated near the llth Street Bridge.
6.4.2 Blair Waterway
Blair Waterway was relatively uncontaminated in comparison with most
other areas examined in Commencement Bay. Sediment toxicity was only observed
at two stations in Segment BLS2 from Lincoln Avenue Drain to the llth Street
Bridge. In general, chemicals in Blair Waterway sediments were either
uniformly or patchily distributed. Concentrations of 4-methylphenol exhibited
an apparent gradient from a maximum near Lincoln Avenue to a minimum toward
the mouth of the waterway. In contrast, 2-methoxyphenol showed an opposite
gradient, indicating possible advective transport into this reach from
areas near the mouth of the waterway. Pentachlorophenol was found in high
concentration at two stations in Blair Waterway (Stations BL-18 and BL-30)
but was not detected in the surrounding sediments. Probably the most unique
feature of sediments in Segment BLS2 was the high EAR for 1,3-dichloro-
benzene. While much higher EAR were observed for other chlorinated benzenes
in other study areas, the highest concentrations of 1,3-dichlorobenzene
were found in Segment BLS2. A clear gradient of decreasing concentrations
was observed in this segment from a maximum at Station BL-19 in the middle
portion of the waterway to a minimum near the mouth. High concentrations
were also found in sediments from the south side of the waterway in Segment
BLS2 (BL-19, BL-20, BL-21, and BL-24). Pentachlorophenol and 1,3-dichloro-
benzene were detected in sediments from only a few other locations in Commence-
ment Bay. There were insufficient biological stations with high concentrations
of these compounds to determine their AET for the study area. A potential
problem area defined by these compounds may extend from about 1,000 ft
east to 500 ft west of Lincoln Avenue in mid-Blair Waterway. This potential
problem area does not have a high priority for source evaluation.
6.27
-------
6.4.3 Siteurn Waterway
A high-priority problem area was defined for all of Sitcum Waterway.
Bioaccumulation of PCBs in fish muscle tissue and a high prevalence of
hepatic neoplasms were major factors that increased the ranking of this
problem area relative to others. Sitcum Waterway sediments differed from
those in neighboring waterways primarily in the much higher EAR for essentially
all of the metals. Based on the most recent samples, metals were present
at high EAR at the head of the waterway and decreased in concentration
toward the mouth. A more patchy distribution of metals is indicated by
historical data. In consideration of all available data, no trends are
evident. However, the concentrations of several metals in both data sets
exceed AET (i.e., arsenic, copper, lead, and zinc). The relative concentrations
of arsenic, copper, lead, and zinc in Sitcum Waterway sediments were similar
to those measured in sediments from the head of City Waterway, except that
arsenic and copper were slightly more enriched in Sitcum Waterway. Most
of the organic compounds were present at low EAR compared with those in
many other areas of Comnencement Bay. Both the LPAH and HPAH had two maxima,
one near the head of the waterway in conjunction with the high EAR for
metals, and one near the mouth at Station SI-14. PCBs were detected in
Sitcum Waterway sediments but concentrations did not exceed either the
80th percentile value for all of Comnencement Bay sediments or the toxicity
or benthic effects AET for PCBs.
6.4.4 Milwaukee Waterway
Milwaukee Waterway was one of the least contaminated areas sampled
in Commencement Bay. The waterway was considered a potential problem area
primarily because of consistently high accumulations of naphthalene in
fish muscle tissues (typically >1,000 ug/kg wet weight), a significant
prevalence of liver lesions, and sediment contamination exceeding Puget
Sound reference area conditions. Elevations of metals in Milwaukee Waterway
sediments were uniformly low. LPAH concentrations decreased slightly from
the head of the waterway to the mouth, and were the only U.S. EPA priority
pollutants with concentrations that exceeded the 80th percentile value
for all Commencement Bay sediments. Concentrations of 2-methoxyphenol
(tentative identification) were high at most stations, possibly representing
material transported from St. Paul Waterway (see Section 6.4.5). Most
of the phenols and chlorinated benzenes (primarily 1,4-dichlorobenzene)
had low EAR and no clear spatial trends in Milwaukee Waterway. Detectable
quantities of 1,3-dichlorobenzene, a comparitively rare compound in Commencement
Bay, were found in the waterway sediments. No substances with high EAR
were observed, and the substances that were detected did not exhibit hot
spots, gradients, or other trends that would indicate a major source in
the waterway. No chemicals exceeded their toxicity or benthic effects
AET in Milwaukee Waterway.
6.4.5 St. Paul Waterway
A high-priority problem area was defined near the mouth of St. Paul
Waterway. Sediment contamination in this problem area differed considerably
from that in all other Commencement Bay areas. None of the HPAH, PCBs,
metals, or chlorinated benzenes were particularly enriched at the site,
6.28
-------
except for limited copper enrichment (below its AET) at Station SP-14,
off the outfall of the Champion International pulp mill. Methylated phenols
(especially 4-methylphenol) and LPAH were the characteristic contaminants
found in the problem area. Concentrations of these compounds all exceeded
toxicity and benthic effects AET near the outfall and decreased abruptly
away from the outfall. Many additional hydrocarbon and substituted phenols
were probably present in these sediments but were not directly measured.
It was apparent from the data from St. Paul and adjacent waterways that
at least 2-methoxyphenol had been transported to other areas of Commencement
Bay.
6.4.6 Middle Waterway
All of Middle Waterway was defined as a second-priority problem area.
Contaminants present in high concentration included copper, arsenic, mercury,
PAH, substituted phenols, and chlorobenzenes. Pentachlorophenol was detected
at the head of the waterway (Station MD-11) at 620 ug/kg DW. This concentration
was similar to that at two stations in Blair Waterway. These three stations
were the only Commencement Bay stations where pentachlorophenol concentra-
tions exceeded 150 ug/kg DW. There were no biological data available from
any of these stations, which limited the analysis of AET for pentachlorophenol.
Few other areas in Commencement Bay had as much diversity in the spectrum
of compounds present at high EAR. Concentrations of copper, arsenic, and
mercury increased regularly from the head to maximum values near the mouth
(Station MD-13), while lead (and to a lesser extent zinc) concentrations
peaked in the middle of the waterway at Station MD-12. The EAR of copper,
arsenic, and mercury were among the highest observed in this study beyond
Segment 2 of the Ruston-Pt. Defiance Shoreline, although arsenic concentrations
were below toxicity and benthic effects AET. Copper and mercury values
exceeded their AET at Station MD-13.
LPAH decreased slightly in concentration from the head to the mouth
of Middle Waterway. LPAH (and HPAH) concentrations exceeded toxicity and
benthic effects AET only at Station MD-11. The highest concentration of
PAH in either the present or historical data set was found at this station.
The composition of these PAH was similar to that observed in City Waterway,
with naphthalene, 2-methylnaphthalene, and phenanthrene exhibiting the
highest EAR. HPAH also decreased in concentration from the head to the
mouth of the waterway but the composition differed along the waterway.
HPAH in sediments near the head and the mouth of the waterway were dominated
by pyrene and benzo(a)pyrene and had low levels of methylpyrenes. Similar
relative concentrations were observed in the Wheeler-Osgood branch of City
Waterway. Sediments from Station MD-12 in the center of the waterway had
higher relative concentrations of methylpyrenes and benzo(a)pyrene than
sediments from the other stations. The relative composition of these compounds
at MD-12 was simlar to that noted in sediments from Station CI-17 in the
middle of City Waterway.
6.4.7 City Waterway
Two high-priority problem areas were defined in City Waterway, one
at the head of the main channel of the waterway, and a second within the
Wheeler-Osgood branch. High EAR for aromatic hydrocarbons, chlorobenzenes,
some metals, and phenols were found in both problem areas. Concentrations
6.29
-------
of these substances also exceeded toxicity and benthic effects AET in these
areas. Within the waterway, lead exhibited one of the most consistent
concentration gradients of any substance in any Commencement Bay study
area. Sediment lead concentrations at the head of the waterway were among
the highest observed beyond Segment 2 of the Ruston-Pt. Defiance Shoreline.
Lead concentrations decreased regularly from a maximum at Station CI-11
to levels comparable with the remaining study area toward the mouth of
the waterway. A similar gradient in percent organic carbon was observed
from the head of the waterway to the mouth. PAH concentrations generally
decreased from the head of the waterway along the main channel of City
Waterway. Maximum PAH concentrations were observed at Station CI-12 rather
than CI-11. Chlorinated benzenes, especially 1,4-dichlorobenzene, were
found at high concentration in the main channel of City Waterway at the
head of the waterway only.
EAR for metals and HPAH in the Wheeler-Osgood problem area were comparable
to those at adjacent stations in the main channel. Selected chlorobenzenes
and 4-methylphenol were found at high concentrations in this problem area,
with clear gradients of decreasing concentrations with distance from the
Wheeler-Osgood branch in the main city waterway channel. These latter
compounds distinguished Wheeler-Osgood from the rest of City Waterway.
The full extent of the possible contamination is uncertain because of the
limited number of samples collected.
A potential hot spot including Stations CI-20 and CI-21 was defined
near the mouth of City Waterway. High levels (but below AET) of 2-methoxyphenol
were present in sediments from the mouth of the waterway, and may have
resulted from transport into the waterway from the St. Paul Waterway problem
area. With the exception of PAH, which were elevated in this area above
their toxicity and benthic effects AET, most other chemicals detected appeared
to be part of a gradient of decreasing concentrations from the middle and
head of City Waterway.
6.4.8 Ruston-Pt. Defiance Shoreline
Sediments within Segment RSS1 of the Ruston-Pt. Defiance Shoreline
were not extensively sampled, but a single station was found to have high
EAR for a few chemicals in an area of otherwise low concentrations. The
concentration gradients observed along the shoreline for most substances
(i.e., PCBs, metals, and at least some of the substituted phenols) were
consistent with transport from other areas as the dominant source of contam-
ination. PAH and 1,4-dichlorobenzene concentrations were elevated at Station
RS-13. An accurate estimate of the spatial extent of the contaminated
area near RS-13 was not possible because of limited sampling.
The most extreme metals contamination in Commencement Bay was found
in the high-priority problem area defined within Segment RSS2. Contamination
of all metals in this problem area was highest at stations directly off
the three outfalls of the ASARCO smelter. It is unclear whether one large
or three smaller, nearshore "hot spots" were present, because samples between
the outfalls were not collected. Concentrations of metals decreased rapidly
both alongshore (toward Stations RS-16 and RS-24) and offshore (toward
Station RS-19 and RS-20). The metals contamination in the "hot spot" defined
within Segment RSS3 off of Pt. Defiance is believed to be associated exclusively
6.30
-------
with slag or spilled ore, because of the granular nature of the sediment.
If the high concentrations found in the problem area within Segment RSS2
were also associated with the smelter slag or ores, then the spatial extent
of the contaminated area could be defined by the physical presence of slag
or ores. However, the high EAR were likely associated with an effluent
component, so the area of extreme EAR associated with this source may be
limited to near the main outfalls. The defined problem area was also highly
contaminated with a number of organic compounds, including PAH, PCBs, and
1,4-dichlorobenzene. The spatial distribution of these compounds was not
as uniform as observed for the metals, but showed variable maxima at each
outfall station. The contaminated area probably extended east from Segment
RSS2 some distance along the shore but did not extend to Station RS-15.
6.5 RANKING OF POTENTIAL PROBLEM CHEMICALS IN PROBLEM AREAS
The previous section described the distributions of major chemical
contaminants that helped distinguish problem areas. This section integrates
results from quantitative relationships developed in Section 4 to prioritize
potential problem chemicals identified in each problem area. The approach
used to reduce the possible list of problem chemicals is shown in Figure 6.4.
Chemicals that were undetected in a problem area were eliminated from con-
sideration as problem chemicals. Some chemicals were detected sporadically.
The detection limit attained for these chemicals was always lower than
the apparent effect thresholds determined in Section 4.1.
Chemicals of concern were defined in Section 3.1 as chemicals with
concentrations exceeding all Puget Sound reference conditions. These chemicals
were not necessarily considered problem chemicals associated with environmental
effects, because most sediments in Commencement Bay were contaminated above
reference conditions and only some of these sediments exhibited toxicity
or benthic effects. As shown in Figure 6.4, chemicals detected at concentra-
tions that exceeded 80 percent of the values determined for all Commence-
ment Bay stations were of greater concern. Source evaluations may be conducted
by WDOE when sediments exceed this level of contamination, even if toxicity
or biological effects are not observed (e.g., Table 6.8 Action-Level
Guidelines).
In all cases, the 80th percentile value for chemicals in Commencement
Bay was lower than the apparent effect threshold defined in Section 4.1.
These thresholds reflected the observation that high levels of some contaminants
were found in sediments that exhibited no observable toxicity or benthic
effects. Because the apparent effect threshold was defined at the contaminant
concentration above which toxicity or benthic effects were always observed,
chemicals present above the threshold are potential problem chemicals (Figure
6.4). Apparent effect thresholds were established for each chemical based
on a data set that included all stations where synoptic chemical, toxicity,
and benthic effects data were collected. For sediments that had no correspond-
ing toxicity or benthic effects data, it was assumed that these same apparent
effect thresholds could be applied to the available chemical data as predictors
of potential problem sediment conditions.
Finally, the highest priority chemicals shown in Figure 6.4 are those
that were present above an AET in a problem area and that also exhibited
a concentration gradient corresponding to observed changes in toxicity
6.31
-------
CHEMICALS DETECTED
u>
ts>
CONCENTRATION EXCEEDS REFERENCE
CONCENTRATION EXCEEDS 80TH PERCENTILE
i
AET EXCEEDED
i
CONCENTRATION GRADIENT CORRESPONDS
TO EFFECTS GRADIENT
CHEMICALS
OF
CONCERN
PROBLEM
CHEMICALS
Figure 6.4. Prioritization of chemicals.
-------
or benthic effects. For example, a strong linear relationship was found
between sediment toxicity in Hylebos Waterway and PCB concentrations (Section
4.2.3). Other contaminants were found above apparent effect thresholds
in the same problem area but none showed as strong a relationship with
the observed toxicity. Therefore, PCBs are potential problem chemicals
with the highest priority for source evaluation in that problem area because
they have a demonstrated correspondence with the observed toxicity. Some
unidentified contaminant with a similar distribution as the PCBs may have
been the actual problem chemical. Source identification for PCBs would
still be recommended based on the assumption that the problem chemical
came from the same source, and that corrective action at the source may
effectively control its release.
Potential problem chemicals in each problem area defined in Table 6.13
are summarized in Table 6.14. Problem areas identified within each segment
listed are ordered in descending rank. Three priorities of chemicals are
given for each problem area. Priority 1 chemicals were present above an
AET and their distributions corresponded with gradients of observed toxicity
or benthic effects. Priority 2 chemicals were also above an AET in the
problem area, but these chemicals either showed no particular relationship
with gradients of observed toxicity or benthic effects, or insufficient
data were available to evaluate their correspondence with gradients. Chemicals
with concentrations that were predicted to be above apparent effect thresholds
at non-biological stations were placed no higher than Priority 2 because
of the lack of biological data. Finally, chemicals with concentrations
above apparent effect thresholds at only one station within the problem
area are shown in Table 6.14 as Priority 3. Problem areas that were small
hot spots often had chemical contamination that exceeded apparent effect
thresholds at only one station. A fourth category of chemicals not shown
in Table 6.14 consisted of all other chemicals with concentrations in the
problem area that exceeded the 80th percentile value for all Commencement
Bay sediments but did not exceed an apparent effect threshold. All measured
chemicals with concentrations (DW) that exceeded the 80th percentile criteria
were summarized in Table 3.15 in at the end of Section 3.
Within each priority group in Table 6.14, chemicals are listed in
descending order of their "toxicity significance factor" (TSF) when a factor
could be determined. Available toxicity significance factors for these
chemicals or chemical groups are listed in Appendix I. These TSF factors
represent a combined index of the potential mammalian toxicity resulting
from the consumption of contaminated seafood and the potential for contaminant
uptake by indigenous organisms. The order of chemicals within a priority
group therefore reflects a first-order approximation of their relative
health hazard.
Priority 1 chemicals were identified in six of the eight highest priority
problem areas (i.e., problem areas exhibiting significant contamination,
toxicity, and benthic effects as well as significant bioaccumulation or
liver lesions in English sole). These chemicals included:
• Mercury, lead, zinc, and arsenic
t PCBs, 4-methylphenol, LPAH, and HPAH.
6.33
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TABLE 6.14. POTENTIAL PROBLEM CHEMICALS IN PROBLEM AREAS
Segment
Containing
Problem Areaa
(in rank order)
Potential Problem Chemicals**
CIS1
HYS2
CIS2
RSS2
Priority 1: Hg, Zn, Pb [TOC<*]C
Priority 2: HPAH, Cd, Ni, Cu, LPAH, 2-methylphenol, 4-methyl-
phenol, phthalate esters [oil & greasejc
Priority 3: dichlorobenzenes, N-nitrosodiphenylamine, [aniline,
benzyl alcohol]0
Priority 1: PCBs
Priority 2: HPAH, Ni , As, tetrachloroethene [Hge, Cue, Zne,
Pbe (intertidal sediments only)]
Priority 3: HCBD, chlorinated benzenes, phthalate esters,
phenol [benzyl alcohol, dibenzothiophene, methyl-
phenanthrenes, methylpyrenes]c
Priority 1: none
Priority 2: HPAH, Cd, Cue, zn f dichlorobenzenes, LPAHe,
Pb, N-nitrosodiphenylamine, 4-methylphenol ,
phenol [biphenyl, TVS, TOC, oil & grease]c
Priority 1: Hg, As, LPAH
Priority 2: HPAH, PCBs, Cd, Ni, Cu, Zn, Pb, Sb [dibenzofuran]C
Priority 3: dichlorobenzenes, N-nitrosodiphenylamine, 2-methyl-
phenol, 4-methylphenol, phthalate esters, [1-methyl-
(2-methylethyl)benzene, biphenyl, dibenzothiophene,
methylphenanthrenes, retene, methylpyrenes]C
SIS1
HYS1
SPS1
Priority 1: none
Priority 2: Ase, Cue, Zn, Pb
Priority 3: N-nitrosodiphenylamine [dibenzofuran, l-methyl-(2-
methylethyl)benzene, diterpenoid hydrocarbons]0,
LPAH, HPAH
Priority 1: HPAH, As, Zn (limited evidence of a gradient
for each with one or more toxicity/effects
indicator)
Priority 2: phenol, Sb
Priority 3: Phthalate esters, ethylbenzene, tetrachloroethene,
[xylenes, 1-methyl-(2-methylethy 1) benzene ,
methylpyrenes, TVS]C
Priority 1: 4-methylphenol
Priority 2: [benzyl alcohol, 1-methyl(2-methylethyl)benzene,
2-methoxyphenol]C
Priority 3: Ni , LPAH, 2-methylphenol, phenol [biphenyl,
diterpenoid hydrocarbons, retene, TVS, TOC]C
6.34
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TABLE 6.14. (Continued)
HYS5 Priority 1: PCBs
Priority 2: HCBD, chlorinated benzenes, chlorinated ethenes
[pentachlorocyclopentane isomer]c, pt>
Priority 3: Hg, HPAH6, Cuez Zne, LPAHe, phenol [benzyl
alcohol, biphenyl "
HYS4
(hotspot)
BLS2
(no action)
CIS3
(hotspot)
MDS1
HYS3
(no action)
BLS1
(no action)
RSS3
(hot spot)
RSS1
(hot spots)
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
none
none
HPAHe, PCBse, HCBD, LPAHe, N-nitrosodiphenylamine
[benzyl alcohol, dibenzofurane^ pentachloro-
cyclopentane isomer, methypyrenes]c
none
dichlorobenzenes, N-nitrosodiphenylamine, 4-methyl-
phenol, phenol
As, HCBD, pentachlorophenol, 2-methylphenol,
oil & grease
none
HPAH, LPAH
PCBse, ine^ phenol [biphenyl, dibenzothiophene]c
none
Hg, Cu
HPAH, As, Zn, dichlorobenzenes, LPAH, pentachloro-
phenol, Pb, 4-methylphenol, phenol [dibenzo-
thiophene, diterpenoid hydrocarbons, methylpyrenes]c
none
PCBs, As, Zn
n-Nitrosodiphenylamine
no toxicity/effects observed at stations tested
none
HPAH, phenol
none
As, Cd, Cu, Zn, Pb, N-nitrosodiphenylamine, Sb
none
none
none
Station RS-13 hotspot: HPAH, dichlorobenzenes,
LPAH, 2-methylphenol, 4-methylphenol [dibenzofuran,
biphenyl, methylphenanthrenes, retene, methyl-
pyrenes]c
Station RS-15 hotspot: As, HCBD, Cd, Ni, Cu,
Zn, phenol (these chemicals exceed AET at RS-15
only after normalization to percent fine-grained
material or to organic carbon content)
6.35
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TABLE 6.14. (Continued)
MIS1 No chemicals found above apparent effect levels at stations
(no action) sampled in Milwaukee Waterway
HYS6
(no action)
BLS3
(no action)
BLS4
(no action)
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
Priority 1:
Priority 2:
Priority 3:
no toxicity/effects observed
none
phthalate esters
at station tested
no toxicity/effects observed at stations tested
none
pentachlorophenol , 2-methyl phenol , 4-methyl phenol
no biological data available
none
phthalate esters
a See Table 6.13 for ranking of problem areas. Problem areas encompass
all stations sampled in 1984 only in Segments HYS1, SIS1, CIS2, RSS2, RSS3,
and possibly MDS1 (Station MD-12 in this segment was close to apparent
effect thresholds for several chemicals).
b Concentrations of these chemicals exceeded an apparent effect threshold
(by various normalizations) in sediment from at least one station in the
defined problem area. Chemicals are listed in each priority group in descending
order of their calculated toxicity significance factor, if available.
Stations with and without biological data area included. Priority 1 chemicals
showed a concentration gradient with toxicity or biological effects gradients.
Priority 2 chemicals were above apparent effect thresholds at more than
one station within the problem area, but either no gradient corresponding
to that for toxicity/effects was observed, or no biological data were available
to assess gradients. Priority 3 chemicals were above apparent effect thresholds
at one station only within the problem area.
c Toxicity significant factors were not available for the chemicals listed
in brackets. These chemicals have not been prioritized relative to other
chemicals in the same priority group.
d TOC concentrations did not exceed an AET in the problem area defined
in Segment CIS1 but the TOC concentration gradient corresponded with observed
changes in effects (e.g., sediment toxicity). This correspondence may
result from the covarying distribution of TOC with other contaminants,
including lead and zinc.
e Chemical elevated above an AET in the defined problem area only on the
basis of historical data.
6.36
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All of these chemicals are recommended for source evaluation. Priority 1
chemicals were not identified in any of the remaining twelve problem areas
with lower priorities for source evaluation. For 10 of these areas, there
were not enough stations to establish correspondence between toxicity or
benthic effects and sediment contamination.
Priority 2 chemicals were identified in all eight of the highest priority
problem areas. Priority 2 chemicals were also identified in three of the
problem areas with lower priorities for source evaluation (i.e., problem
areas within Segments BLS2, CIS3, and RSS3). In addition to the chemicals
listed as Priority 1, these included:
• Cadmium, nickel, and antimony
• HCBD, chlorinated benzenes, chlorinated ethenes, phenol,
2-methylphenol, N-nitrosodiphenylamine, dibenzofuran, and
selected phthalate esters (e.g., bis-(2-ethylhexyl) and
di-n-butyl phthalates)
• Selected tentatively identified compounds.
These chemicals are recommended for source evaluation where sufficient
spatial data are available to indicate sources. Priority 3 chemicals were
identified in each problem area except Milwaukee Waterway and Segments
CIS2 (City Waterway) and RSS3 (Pt. Defiance-Ruston Shoreline). The latter
two problem areas had no Priority 3 chemicals because all potential problem
chemicals were elevated at more than one station in the problem area.
The potential problem area in Milwaukee Waterway had no chemicals elevated
above an AET. Priority 3 chemicals not already included in the Priority 2
group are: pentachlorophenol, aniline, and selected tentatively identified
compounds. These chemicals are not recommended for source identification
unless their occurrence at a single station in a problem area is associated
with a potential source that is not necessarily indicated by other chemicals
(e.g. pentachlorophenol in the problem area within Segment BLS2). Priority 2
and 3 chemicals with spatial distributions that are poorly defined are
still recommended for potential source identification when additional concern
has been placed on their potential for effects in fish (e.g., accumulations
of benzyl alcohol in fish livers discussed in Section 4.6.2).
Chemicals present below apparent effect thresholds but above the 80th
percent value for all Commencement Bay sediments are recommended for source
identification when they appear to be highly characteristic of a particular
problem area and potential sources (e.g., TOC at the head of City Waterway).
6.6 SUMMARY
Fourteen problem areas (including isolated "hot spots") were recommended
for priority source evaluation. The remaining 7 of the total 21 problem
areas identified were not recommended for high priority source evaluation.
Six of these lowest priority areas contained stations where contaminant
concentrations exceeded AET, but no confirming biological data were available.
The seventh area not recommended for priority source evaluation (Milwaukee
Waterway) contained no chemicals measured above their AET.
6.37
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Potential problem chemicals of varying priorities for source identification
were also identified in each of the 14 areas recommended for priority source
evaluation. Eight problem areas have the highest priority for immediate
source evaluation. These problem areas are located in Hylebos, City, Sitcum,
and St. Paul Waterways and along the Ruston-Pt. Defiance Shoreline. Eight
problem chemicals were identified in six of these latter problem areas
that have the highest priority for source identification because of apparent
correspondences with observed toxicity or benthic effects.
6.38
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