Commencement Bay Nearshore, Tideflats Remedial Investigation Final Report


TC-3752
FINAL REPORT
EPA-910/9-85-134b
COMMENCEMENT BAY
NEARSHORE / TIDEFLATS
REMEDIAL INVESTIGATION
VOLUME 2



I

AUGUST, 1985
PREPARED FOR:
WASHINGTON STATE DEPARTMENT OF ECOLOGY
AND U.S. ENVIRONMENTAL PROTECTION AGENCY
Mr. James D. Krull, Project Manager
Washington State Department of Ecology
Olympia, Washington

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TC-3752
Final Report
COMMENCEMENT BAY NEARSHORE/
TIDEFLATS REMEDIAL INVESTIGATION
Volume 2
by
Tetra Tech, Inc.
for
Washington State Department of Ecology
U.S. Environmental Protection Agency
Mr. James D. Krull, 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 VOLUME 2
Page
LIST OF FIGURES	iv
LIST OF TABLES	xi
CONTENTS VOLUME I	xiv
7.0	SOURCE EVALUATION	7.1
7.1	INTRODUCTION	7.1
7.2	HYLEBOS WATERWAY	7.5
7.2.1	Introduction	7.5
7.2.2	Contaminants of Concern	7.8
7.2.3	Polychlorinated Biphenyls	7.13
7.2.4	Aromatic Hydrocarbons	7.22
7.2.5	Dibenzofuran	7.38
7.2.6	Benzyl Alcohol	7.40
7.2.7	Chlorinated Hydrocarbons	7.43
7.2.8	Pentachlorocyclopentane Isomer	7.73
7.2.9	Arsenic	7.76
7.2.10	Copper, Lead, and Zinc	7.84
7.2.11	Mercury	7.106
7.2.12	Hylebos Waterway: Summary and Recommendations	7.110
7.3	SITCUM WATERWAY	7.115
7.3.1	Introduction	7.115
7.3.2	Aromatic Hydrocarbons and Dibenzofuran	7.119
7.3.3	Metals	7.124
7.4	ST. PAUL WATERWAY	7.138
7.4.1	Introduction	7.138
7.4.2	Spatial Distribution	7.142
7.4.3	Loading Estimates	7.150
7.4.4	Source Identification	7.153
7.4.5	Summary and Recommendations	7.159
7.5	MIDDLE WATERWAY	7.160
7.5.1	Introduction	7.160
7.5.2	Pentachlorophenol and Dichlorobenzenes	7.164
7.5.3	Aromatic Hydrocarbons and Dibenzofuran	7.169
7.5.4	Mercury and Copper	7.173
7.5.5	Middle Waterway: Summary and Recommendations	7.179
ii

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7.6 CITY WATERWAY	7.181
7.7
7.6.1
Introduction
7.181
7.6.2
Contaminants of Concern
7.183
7.6.3
Organic Enrichment
7.190
7.6.4
Aromatic Hydrocarbons and Dibenzofuran
7.197
7.6.5
Dichlorobenzenes
7.209
7.6.6
4-Methylphenol
7.217
7.6.7
Polychlorinated Biphenyls
7.223
7.6.8
Copper and Zinc
7.227
7.6.9
Lead
7.236
7.6.10
Summary and Recommendations
7.241
RUSTON'
-PT. DEFIANCE SHORELINE
7.244
7.7.1
Introduction
7.244
7.7.2
Spatial Distribution
7.249
7.7.3
Loading Estimates
7.262
7.7.4
Source Identification
7.266
7.7.5
Summary and Recommendations
7.277
8.0 RECOMMENDATIONS OF AREAS AND SOURCES FOR POTENTIAL REMEDIAL
ACTIONS
8.1
8.1 INTRODUCTION
8.1
8.2 RECOMMENDATIONS FOR REMEDIAL ACTION
8.4
8.2.1	Hylebos Waterway
8.2.2	Sitcum Waterway
8.2.3	St. Paul Waterway
8.2.4	Middle Waterway
8.2.5	City Waterway
8.2.6	Ruston - Pt. Defiance Shoreline
8.4
8.5
8.5
8.6
8.6
8.7
8.3 GENERAL RECOMMENDATIONS
8.7
9.0 OVERVIEW OF CONTAMINATION AND BIOLOGICAL	EFFECTS IN
COMMENCEMENT BAY	9-!
10.0 STUDY DESIGN EVALUATION AND RECOMMENDATIONS FOR FUTURE STUDIES 10.1
10.1	SEDIMENT CHEMISTRY	I0-1
10.2	BIOLOGICAL EFFECTS	10.2
10.3	DECISION-MAKING APPROACH	10.4
10.4	SOURCE IDENTIFICATION	10.5
11.0 REFERENCES	11-1
ill

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FIGURES
Number	Page
7.1.1 Problem areas and their respective contaminants of concern
for which source identification has been pursued	7.3
7.2.1	Major industries surrounding the Hylebos Waterway from
Port of Tacoma - summary of port services, facilities,
and industries	7.6
7.2.2	Discharges to the Hylebos Waterway noted in the text and
their locations along the waterfront	7.7
7.2.3	Dredging activity in the Hylebos Waterway	7.9
7.2.4	Surficial sediment stations and sediment core locations
from all Hylebos Waterway studies in the project database 7.10
7.2.5	Areas of Hylebos Waterway with the greatest concentrations
of each contaminant of concern in the surficial sediments 7.12
7.2.6	Concentrations of total PCBs in the surficial sediments
of the Hylebos Waterway with distance from the mouth of
the waterway	7.14
7.2.7	Concentrations of total PCBs in the surficial sediments
of the Hylebos Waterway Segment 5	7.15
7.2.8	Concentrations of total PCBs with depth in the sediment
column	7.17
7.2.9	Concentrations of total PCBs in the surficial sediments
of Hylebos Waterway Segments 2 and 3	7.18
7.2.10	Concentrations of total PCBs with depth in the sediment
column
7.2.11	Concentrations of total low molecular weight polycyclic
aromatic hydrocarbons in the surficial sediments of the
Hylebos Waterway with distance from the mouth of the
waterway	7.23
7.2.12	Surficial sediment concentrations of LPAH in Hylebos
Waterway	7.24
7.2.13	Concentrations of total high molecular weight polycyclic
aromatic hydrocarbons in the surficial sediments of the
Hylebos Waterway with distance from the mouth of the
waterway	7.26
iv

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7.2.14	Surficial sediment concentrations of HPAH in Hylebos
Waterway	7.27
7.2.15	Ratio of the concentrations of total high molecular weight
PAH to total low molecular weight PAH at all Tetra Tech
survey stations in the Hylebos Waterway	7.28
7.2.16	Concentrations of PAH with depth in the sediment column 7.29
7.2.17	Concentrations of dibenzofuran in the surficial sediments
of the Hylebos Waterway with distance from the mouth of the
waterway	7.39
7.2.18	Concentrations of benzyl alcohol in the surficial sediments
of the Hylebos Waterway with distance from the mouth of the
waterway	7.41
7.2.19	Concentrations of hexachlorobenzene in the surficial
sediments of the Hylebos Waterway with distance from the
mouth of the waterway	7.44
7.2.20	Concentrations of 1,4-dichlorobenzene in the surficial
sediments of the Hylebos Waterway with distance from the
mouth of the waterway	7.45
7.2.21	Concentrations of hexachlorobenzene in the surficial
sediments of Hylebos Segment 5	7.46
7.2.22	Concentrations of total chlorinated butadienes in the
surficial sediments of the Hylebos Waterway with distance
from the mouth of the waterway	7.47
7.2.23	Concentrations of hexachlorobutadiene in the surficial
sediments of the Hylebos Waterway with distance from the
mouth of the waterway	7.48
7.2.24	Concentrations of tetrachloroethene in the surficial
sediments of the Hylebos Waterway with distance from the
mouth of the waterway	7.49
7.2.25	Concentrations of chlorinated butadienes with depth in the
sediment column	7.51
7.2.26	Concentrations of chlorinated benzenes with depth in the
sediment column	7.52
7.2.27	Flow schematic of chlorine production and chlorinated
organic waste handling at Occidental Chemical Corporation 7.60
7.2.28	Location of groundwater monitoring wells at Occidental
Chemical Corporation	7 54
v

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7.2.29	Concentration of chlorinated organic compounds in ground-
water beneath Occidental Chemical Corporation	7.65
7.2.30	Concentrations of tetrachloroethene in groundwater monit-
oring wells on the property of Pennwalt Corporation	7.66
7.2.31	Relationship between chloroform and tetrachloroethene
concentrations in groundwater beneath the Pennwalt property 7.69
7.2.32	Concentrations of pentachlorocyclopentane in the surficial
sediments of the Hylebos Waterway with distance from the
mouth of the waterway	7.74
7.2.33	Concentrations of arsenic in the surficial sediments of
the Hylebos Waterway with distance from the mouth of the
waterway	7.77
7.2.34	Concentrations of copper in the surficial sediments of
the Hylebos Waterway with distance from the mouth of the
waterway	7.85
7.2.35	Concentrations of lead in the surficial sediments of the
Hylebos Waterway with distance from the mouth of the
waterway	7.86
7.2.36	Concentrations of zinc in the surficial sediments of the
Hylebos Waterway with distance from the mouth of the
waterway	7.87
7.2.37	Concentrations of nickel in the surficial sediments of
the Hylebos Waterway with distance from the mouth of the
waterway	7.89
7.2.38	Concentrations of metals with depth in the sediment column 7.90
7.2.39	Concentrations of mercury in the surficial sediments of
the Hylebos Waterway with distance from the mouth of the
waterway	7.107
7.2.40	Sources of contaminants to the Hylebos Waterway	7.111
7.3.1	Industries within the Sitcum Waterway drainage area	7.117
7.3.2	Surficial sediment stations and the sediment core
location from all studies in Sitcum Waterway	7.118
7.3.3	Concentrations of low molecular weight PAH in
surficial sediments of Sitcum Waterway	7.120
7.3.4	Concentrations of high molecular weight PAH in
surficial sediments of Sitcum Waterway	7.121
vi

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7.3.5	Concentrations of dibenzofuran in surficial
sediments of Sitcum Waterway	7.122
7.3.6	Concentrations of copper in surficial sediments
of Sitcum Waterway	7.125
7.3.7	Concentrations of zinc in surficial sediments of
Sitcum Waterway	7.126
7.3.8	Concentrations of lead in surficial sediments of
Sitcum Waterway	7.127
7.3.9	Concentrations of arsenic in surficial sediments
of Sitcum Waterway	7.129
7.4.1	Major industries and discharges to the St. Paul Waterway 7.139
7.4.2	Surficial sediment stations and sediment core locations
from all studies in the St. Paul Waterway	7.141
7.4.3	Concentrations of total organic carbon (%) in the
surficial sediments of the St. Paul Waterway	7.143
7.4.4	Concentrations of 4-methylphenol in the surficial sediments
of the St. Paul Waterway	7.144
7.4.5	Concentrations of 2-methoxyphenol in the surficial sediments
of the St. Paul Waterway	7.145
7.4.6	Concentrations of l-methyl-2-(lmethylethyl)benzene in the
surficial sediments of the St. Paul Waterway	7.146
7.4.7	Concentrations of naphthalene in the surficial sediments
of the St. Paul Waterway	7.147
7.4.8	Concentrations of 2-methylnaphthalene in the surficial
sediments of the St. Paul Waterway	7.148
7.4.9	Concentrations of copper in the surficial sediments of the
St. Paul Waterway	7.149
7.5.1	Major industries and discharges to the Middle Waterway	7.161
7.5.2	Surficial sediment stations and sediment core locations
from all studies in Middle Waterway	7.163
7.5.3	Concentrations of pentachlorophenol in the surficial
sediments of the Middle Waterway	7.165
7.5.4	Concentrations of 1,4-dichlorobenzene in the surficial
sediments of Middle Waterway	7.166
7.5.5	Concentrations of low molecular weight PAH in the surficial
sediments of Middle Waterway	7.170
vii

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7.5.6	Concentrations of high molecular weight PAH in the
surficial sediments of Middle Waterway	7.171
7.5.7	Concentrations of dibenzofuran in the surficial sediments
of Middle Waterway	7.172
7.5.8	Concentrations of copper in the surficial sediments of
Middle Waterway	7.174
7.5.9	Concentrations of mercury in the surficial sediments of
Middle Waterway	7.175
7.6.1	Industries surrounding City Waterway	7.182
7.6.2	Stormdrain locations and NPDES permitted discharge locations
in City Waterway	7.185
7.6.3	Surficial sediment stations and sediment core locations
from all studies in City Waterway	7.186
7.6.4	Areas of City Waterway with the greatest concentrations
of each contaminant of concern in the surficial sediments 7.189
7.6.5	Surficial sediment concentrations of total organic carbon
in City Waterway	7.191
7.6.6	Percentage of total organic carbon with depth in sediments
of City Waterway	7.192
7.6.7	Surficial sediment concentrations of LPAH in City Waterway 7.198
7.6.8	Surficial sediment concentrations of HPAH in City Waterway 7.199
7.6.9	Concentration of total LPAH on a dry weight basis with
depth in sediments of City Waterway	7.201
7.6.10	Concentration of total HPAH on a dry weight basis with
depth in sediments of City Waterway	7.202
7.6.11	Surficial sediment concentrations of 1,4-dichlorobenzene
in City Waterway	7.210
7.6.12	Surficial sediment concentrations of 1,2-dichlorobenzene
in City Waterway	7.211
7.6.13	Concentrations of 1,2-dichlorobenzene and 1,4-dichloro-
benzene with depth in the sediment column	7.213
7.6.14	Surficial sediment concentrations of 4-methylphenol in
City Waterway	7.218
7.6.15	Concentration of 4-methylphenol with depth in the sediment
column at stations in City Waterway	7.219
viii

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7.6.16	Surficial sediment concentrations of PCBs in City Waterway 7.224
7.6.17	Concentration of PCBs with depth in the sediment at
Station CI-60, G05 near the head of City Waterway	7.225
7.7.18	Surficial sediment concentrations of (A) copper, and (B)
zinc in City Waterway	7.228
7.6.19	Concentration of (A) copper, and (B) zinc with depth of
sediment at Station CI-60, G05 near the head of City
Waterway	7.229
7.6.20	Approximate drainage area served by the Nalley Valley
and south Tacoma drains	7.233
7.6.21	Surficial sediment concentrations of lead in City Waterway 7.237
7.6.22	Concentration of lead with depth in the sediment at
Station CI-60, G05 near the head of City Waterway	7.238
7.6.23	Locations of known and potential sources of contaminants to
City Waterway	7.242
7.7.1	Major industries and discharges to the Ruston Shoreline 7.245
7.7.2	Surficial sediment stations and sediment core locations
from all studies on the Ruston Shoreline	7.248
7.7.3	Concentrations of arsenic in the surficial sediments of
the Ruston Shoreline	7.250
7.7.4	Concentrations of cadmium in the surficial sediments
of the Ruston Shoreline	7.251
7.7.5	Concentrations of copper in the surficial sediments
of the Ruston Shoreline	7.252
7.7.6	Concentrations of lead in the surficial sediments
of the Ruston Shoreline	7.253
7.7.7	Concentrations of mercury in the surficial sediments
of the Ruston Shoreline	7.254
7.7.8	Concentrations of zinc in the surficial sediments
of the Ruston Shoreline	7.255
7.7.9	Concentrations of low molecular weight PAH in the
surficial sediments of the Ruston Shoreline	7.256
7.7.10	Concentrations of high molecular weight PAH in the
surficial sediments of the Ruston Shoreline	7.257
ix

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7.7.11	Concentrations of dibenzofuran in the surficial
sediments of the Ruston Shoreline	7.258
7.7.12	Concentrations of 2-methyl phenol in the surficial
sediments of the Ruston Shoreline	7.259
7.7.13	Concentrations of 1,4-dichlorobenzene in the
surficial sediments of the Ruston Shoreline	7.260
7.7.14	Concentrations of PCBs in the surficial sediments of
Ruston Shoreline	7.261
x

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LIST OF TABLES
Number	Page
7.2.1	Discharges to the Hylebos Waterway in which PCBs
have been undetected	7.21
7.2.2	Discharges to the Hylebos Waterway in which PAH
have been undetected	7.31
7.2.3	Potential industrial sources of polycylic aromatic
hydrocarbons in Hylebos Segments 4 and 5	7.33
7.2.4	Chlorinated ethenes: summary of loadings from
discharges to Hylebos Waterway	7.54
7.2.5	Chlorinated benzenes and butadienes: summary of
loadings from discharges to Hylebos Waterway	7.56
7.2.6	AWARE (1981) groundwater samples containing chloroform
and/or tetrachloroethene concentrations above
detection limits	7.68
7.2.7	Arsenic: summary of loadings from discharges to
Hylebos Waterway	7.78
7.2.8	Copper: summary of loadings from discharges to
Hylebos Waterway	7.92
7.2.9	Lead: summary of loadings from discharges to Hylebos
Waterway	7.95
7.2.10	Zinc: summary of loadings from discharges to Hylebos
Waterway	7.98
7.2.11	Mercury: summary of loadings from discharges to
Hylebos Waterway	7.108
7.3.1	Dredging history of Sitcum Waterway	7.116
7.3.2	Concentrations of arsenic and metals with depth in the
sediment	7.130
7.3.3	Arsenic: summary of loadings from discharges to the
Sitcum Waterway	7.131
7.3.4	Copper: summary of loadings from discharges to the
Sitcum Waterway	7.132
XI

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7.3.5	Lead: summary of loadings from discharges to the
Siteurn Waterway	7.133
7.3.6	Zinc: summary of loadings from discharges to the
Site urn Waterway	7.134
7.4.1	Concentration of the contaminants of concern with depth
in the sediment	7.151
7.4.2	BOD, COD, and total suspended solids: summary of
loadings from discharges to the St. Paul Waterway and
from the Puyallup River	7.152
7.4.3	Naphthalene and copper: summary of loadings from
discharges to the St. Paul Waterway and from the
Puyallup River	7.154
7.5.1 Comparison of arsenic and metal ratios in Middle
Waterway sediments	7.178
7.6.1	Summary of dredging projects, City Waterway	7.184
7.6.2	COD: summary of loadings from discharges to City Waterway 7.194
7.6.3	Ratio of high molecular weight PAH to low molecular
weight PAH with depth in sediments of City Waterway	7.204
7.6.4	Low molecular weight PAH: summary of loadings from
discharges to the City Waterway	7.205
7.6.5	High molecular weight PAH: summary of loadings from
discharges to the City Waterway	7.206
7.6.6	Copper: summary of loadings from discharges to the
City Waterway	7.230
7.6.7	Zinc: summary of loadings from discharges to the
City Waterway	7.231
7.6.8	Lead: summary of loadings from discharges to the
City Waterway	7.239
7.7.1	Summary of dredging projects, Ruston-Pt. Defiance
Shoreline	7.246
7.7.2	Concentrations of organic compounds with depth in the
sediment	7.263
7.7.3	Concentrations of arsenic and metals with depth in the
sediment	7.264
7.7.4	Organic compounds: summary of loadings from discharges
along the Ruston Shoreline	7.265
xii

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7.5	Arsenic: summary of loadings from discharges along
the Ruston Shoreline	7.267
7.6	Cadmium: summary of loadings from discharges along
the Ruston Shoreline	7.268
7.7	Copper and mercury: summary of loadings from discharges
along the Ruston Shoreline	7.269
7.8	Lead: summary of loadings from discharges along the
Ruston Shoreline	7.270
7.9	Zinc: summary of loadings from discharges along the
Ruston Shoreline	7.271
1	Final ranking of problem areas	8.2
xiii

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CONTENTS VOLUME 1
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
xiv

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2.5
SEDIMENT BIOASSAYS
2.29

2.5.1	Field Sampling
2.5.2	Laboratory Analysis
2.29
2.29
2.6
FISH HISTOPATHOLOGY
2.32

2.6.1	Field Sampling
2.6.2	Histopathological Examination
2.32
2.33
2.7
BIOACCUMULATION
2.33

2.7.1	Field Sampling
2.7.2	Laboratory Analysis for Metals
2.7.3	Laboratory Analysis for Organic Compounds
2.33
2.34
2.35
2.8
DATA MANAGEMENT
2.36

2.8.1	The Database
2.8.2	Data Analysis
2.8.3	Graphics
2.8.4	Quality Control
2.8.5	Library
2.36
2.37
2.37
2.38
2.38
2.9
HEALTH AND SAFETY
2.38
2.10
SAMPLING AND ANALYSIS QA/QC
2.39

2.10.1	Sample Collection
2.10.2	Organic Compound Analyses
2.10.3	Trace Metals and Ancillary Analyses
2.10.4	Benthic Macroinvertebrates, Sediment Bioassays,
and Fish Histopathology
2.39
2.40
2.41
2.41
2.11
RISK ASSESSMENT
2.41

2.11.1	Exposure Evaluation
2.11.2	Health Effects (Hazard Assessment) Methodology
2.11.3	Risk Assessment Calculations
2.44
2.47
2.47
2.12 SOURCE IDENTIFICATION
2.12.1	Sediment Chemistry
2.12.2	Water Quality Data
2.12.3	Point Sources and Runoff
2.12.4	Groundwater Sources
2.12.5	Atmospheric Sources
2.12.6	Spills
2.12.7	Dredging

2.52
2.52
2.57
2.57
2.62
2.63
2.63
2.64

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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*142
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 HIST0PATH0L0GY	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
xv i

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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
xvii

-------
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
xviii

-------
7.0 SOURCE EVALUATIONS
7.1 INTRODUCTION
Results of Task 4 of the Commencement Bay Nearshore/Tideflats Remedial
Investigation are presented in Section 7. The primary goal of Task 4 was
to determine major sources of contaminants observed in the surficial sediments
of the nearshore/tideflats area. This was a difficult task given the extensive
industrial development of the Tacoma area over the past century. Throughout
this period, Commencement Bay and associated waterways have received contam-
inants from a multitude of discharges, many of which, until recently, have
been unregulated. Even today, major discharges are not routinely monitored
or regulated for many of the contaminants identified to be of concern in
these investigations.
The nearshore/tideflats area of Commencement Bay has been more intensively
sampled than any other in Puget Sound. Therefore, a large database was
available on potential contaminant sources and observed contaminant levels
in water and sediment. Ancillary information was also available. Some
of the most valuable information utilized in source identification included:
•	Spatial gradients of contamination in surficial sediments -
The spatial gradient of sediment contamination was the most
important component of source identification. It was used
to establish the probable location of the contaminant source,
with the implicit assumption that the most contaminated
sediments were closest to the source.
t Vertical gradients of contamination in sediment cores -
This information was used to determine the history of contaminant
input. Correlations between sediment concentrations and
historical land use information were used to identify past
sources of contamination.
•	Analyses for the contaminant in discharges - Effluents from
many point and nonpoint sources in the nearshore/tideflats
area have been analyzed for some of the contaminants of
concern. This information was used to identify potential
sources, to determine if known sources could account for
the contaminant levels seen in the sediments, and to calculate
mass loading by which sources could be ranked.
•	Dredging history - Knowledge of past dredging activities
was valuable in interpreting patterns of contamination seen
in surficial and subsurface sediments.
•	Environmental fate processes - Information on environmental
fate process (e.g., solubility, sorption, volatilization,
degradation) of the various contaminants was valuable in
7.1

-------
placing constraints on the timing or route of contaminant
migration.
• Industrial activities - When the spatial gradient of contami-
nation suggested a specific property as the contaminant
source, past and present industrial activities at the site
were reviewed to confirm responsibility. This review included
period of operation, raw materials, manufacturing processes,
potential by-products, waste disposal practices, past spills,
and the history of enforcement actions.
Source identifications were attempted for preliminary contaminants
of concern in problem areas defined on the basis of significant chemical,
toxicity, and biological indicators. The twelve priority problem areas
for which source identifications were conducted are shown in Figure 7.1.1.
A preliminary, incomplete set of contaminants was defined for these investi-
gations because project time constraints required source evaluations to
begin several months before all data analyses in Task 3 investigations
were completed. Contaminants designated on a preliminary basis for these
source evaluations are summarized in Figure 7.1.1 for each problem area.
The preliminary list of contaminants in Figure 7.1.1 was based on
chemicals with concentrations that exceeded 80 percent of all sediment
concentrations in the Commencement Bay study area at more than one station
in a problem area. Because of the large number of source identifications
required using this guideline, not all chemicals present above the 80th
percentile level were included on the preliminary list for source identifica-
tion. Contaminants exceeding the 80th percentile concentration cutoff
were excluded from the preliminary list when their spatial distributions
were clearly unrelated to the observed pattern of toxicity or biological
effects in a problem area, or when there were several other chemicals with
clearer relationships. Chemicals present below the 80th percentile concentra-
tion in a problem area were included on the preliminary list if there was
a concern for potential biological effects in the corresponding waterway
(e.g., elevated benzyl alcohol concentrations in abnormal fish livers or
PCBs in fish muscle tissue).
Chemicals found in high concentration only in historically sampled
sediments in a problem area were not always included in the preliminary
list of potential problem chemicals because these data sets had not yet
been fully incorporated into the data analysis (in some cases, these data
were not received from the contributing agencies until after source evaluations
had begun). Chemicals later determined to have the highest priority for
source evaluation were already on the preliminary list of potential problem
chemicals. These chemicals were present above an Apparent Effect Threshold
(AET) in a problem area and had concentration gradients that corresponded
with observed toxicity or benthlc effects as discussed in Section 6 (Volume
I). Most chemicals determined in Section 6 as having the second highest
priority for source evaluation were also already on the preliminary list
of potential problem chemicals. These second priority contaminants were
defined as those with concentrations above an AET at more than one station
within a problem area, but either their concentration gradient did not
correspond with observed toxicity or benthic effects, or there were insufficient
data to evaluate the relationships. Priority chemicals that had not been
7.2

-------
PCBs
Chlorinated ethenes
Chlorinated benzenes
Chlorinated butadienes
Pentachlorocyclopentane
Mercury
Araaatic hydrocarbons
(low I high Molecular wt)
Dibenzofuran
PCBs
Arsenic
Cadmium
Copper
Lead
Mercury
Zinc
Aromatic hydrocarbons
(low l high molecular wt)
PCBs
Chlorinated benzenes
Chlorinated butadienes
I
Aromatic Hydrocarbons
(low t high molecular wt)
Dibenzofuran
Arsenic
Copper
Lead
Zinc
Alkylated phenols
Methoxyphenols
Naphthalene
Methylnaphthalenes
Methylisopropylbenzene
Copper
Organic enrichment
Aromatic hydrocarbons
(low ( high molecular wt)
Dibenzofuran
Dichiorobenzenes
Pen tachlorophenol
Copper
Mercury
Aromatic hydrocarbons
(low t high molecular wt)
Dibenzofuran
PCBs
Chlorinated ethanes
Chlorinated benzenes
Chlorinated butadienes
Benzyl alcohol
Aromatic hydrocarbons
(low I high molecular wt)
Phenols
Chlorinated benzenes
Arsenic
Copper
Lead
Mercury
Aromatic hydrocarbons
I low ( high molecular art)
Dibenzofuran
1,4-Dichlorabenzane
< Methylphenol
Copper
Lead
scale (in
Aromatic hydrocarbons
(low t high molecular wt)
Dibenzofuran
1,4-Dichlorobenzene
t-Methyl phenol
PCBs
Lead
Zinc
Copper
Organic enrichment
Aromatic hydrocarbons
(low ( high molecular wt)
Arsenic
Copper
Lead
Zinc
Aromatic hydrocarbons
(low ( high molecular wt)
Dichiorobenzenes
Organic enrichment
Figure 7.1.1
PROBLEM AREAS (SHADED) AND THEIR RESPECTIVE CONTAMINANTS OF CONCERN
FOR WHICH SOURCE IDENTIFICATION HAS BEEN PURSUED

-------
subjected to source evaluation as preliminary contaminants of concern are
summarized at the beginning of each major section. A complete list of
priority chemicals in each problem area is given in Table 6.14 in Section
6. For ease of comparison, AET for different chemicals are noted on spatial
and depth plots of contaminant concentrations.
The remainder of Section 7.0 is directed towards identifying potentially
responsible sources for each preliminary contaminant of concern within
each problem area shown on Figure 7.1.1. For each potential source that
is identified, the following additional information is provided, if available:
t Characterization of the source as historical or ongoing
•	Potential routes of contaminant migration
•	Ranking of the source relative to others in the problem
area, if permitted by the mass loading estimates
•	Ongoing remedial actions, if any
•	Data gaps
•	Recommendations for source control and, if possible, a statement
on the effectiveness of this control in improving sediment
quality.
The results are presented in the following order: Section 7.2 - Hylebos
Waterway; 7.3 - Sitcum Waterway; 7.4 - St. Paul Waterway; 7.5 - Middle
Waterway; 7.6 - City Waterway; and 7.7 - Ruston-Pt. Defiance Shoreline.
Metal concentration data normalized to percent fine-grained material are
presented only when additional trends apparent in the dry-weight data are
observed. These normalizations are not used in the discussion of Hylebos
Waterway because the required grain size data are missing for key samples.
7.4

-------
HYLEBOS WATERWAY
7.2 HYLEBOS WATERWAY
7.2.1 Introduction
7.2.1.1	Industrial Development--
Hylebos Waterway was formed by dredging the Puyallup River delta in
the early 1920s. Since that time, its shoreline has become heavily indus-
trialized (Figure 7.2.1). Among the first industries established along
Hylebos Waterway were Occidental Chemical Corporation (previously Hooker
Chemical and Plastics Corporation) and Pennwalt Corporation (previously
Pennsylvania Salt Manufacturing Company). These industries began operations
along Hylebos Waterway in the 1920s to provide chlorine for local pulp
and paper industries. In the past, they produced a variety of inorganic
compounds (e.g., sodium hypochlorite and caustic soda) and continue to
do so. Schaffer Box and Pulp operated along the south shore of the waterway
from 1924 to 1932. As a result of discharge of their sulfite waste liquipr,
they have been implicated as a major source of pollution during that time
(Dames and Moore 1982).
Two smelting industries were established along upper Hylebos Waterway
in the early 1940s. Ohio Ferro Alloys was built in 1942 for the production
of chrome, and later silicate and ferrosi1icate, on the site of what is
now Cascade Timber Yard #2. The plant closed in 1972 and has since been
razed (Dames and Moore 1982). In 1941-42, Kalunite Inc./Oline Co. opened
an aluminum smelting plant on the site of what is now Kaiser Aluminum and
Chemical Corporation, which took over operation of the plant in 1949.
Industrial development along the north shore of Hylebos Waterway has
not been as extensive as that along the south shore, due principally to
the limited land area available between the waterway and the steep bluffs.
The three largest industries along the north shore are Sound Refining,
General Metals, and Tacoma Boatbuilding. All three were established at
their present location in the late 1960s to mid-1970s.
A notable feature of Hylebos Waterway is the numerous log sorting
yards along its shoreline. Log sorting yards occupy nearly all of the
southern shoreline of the upper waterway and several areas throughout the
middle portion of the waterway. ASARCO slag has been used as ballast in
most of these yards and surface water runoff from the yards has been found
to contain high concentrations of metals (Norton and Johnson 1985a).
7.2.1.2	Discharges-
Locations of all discharges to Hylebos Waterway that are noted in
the text are shown in Figure 7.2.2. The common names for these discharges
are given when available. Several of the discharges are regulated and
are authorized discharges through the National Pollutant Discharge Elimination
System (NPDES) permit program. Four of the permitted discharges have been
classified as major industrial discharges: Occidental Chemical Corpora-
tion, Pennwalt Corporation, Kaiser Aluminum and Chemical Corporation, and
7.5

-------
ienM
Chemical
Tacoma
Boatbuilding
Gararal Mataf*
Inc.
upper
Turning
Battn
Lower
Turning
Bailn
8
oodworfcln
SEGMENT 1
SEGMENT
SEGMENT 2 m
Dunlap
Tewing
LA Pacific
Woodworking
Pacific
Taylor Way
SECMENT 5
City of
Tecana / Cham toil
PftCMMM
Port of
Alexander Avenue
Figure 7.2.1
MAJOR INDUSTRIES SURROUNDING THE HYLEBOS WATERWAY
FROM PORT OF TACOMA - SUMMARY OF PORT SERVICES, FACILITIES AND INDUSTRIES
7.6

-------
HY-704
Sound
defining
WOES NAOOOJ2M
HM-OJI
n Momlngi
| Ditch
1 HY-028
f ?!
KCMENT 2
12000
3000
SEGMENT J
HC-000
Kyfaboa
Hr-051
Pannwalt
Corporation
NFOes WA 0001113
HY -070
Buffricn
Woodworking
NPDCS WV0002321
HY-050
_5*"
Chnmal
Bitch

ZIMf \ [
Dismantling)
HY-0M
Lincoln
Avanua
Drain
KT-092
NTOE5 WAM37US
«l £
HK-M2
Kalaar
Ditch
Kala«p
Aluminum
• ChMksl
Corporation
MOB WAOOOOI31
HY-707
Occldantal
Chamlcat
Corporation ,
NPDCS MMI72H
HY-002
U.S.
Cypvum
KRXS VR0003S22
Figure 7.2.2
DISH^S£,S 70 THE MYLEB0S waterway noted in the text and their locations
ALONG THE WATERFRONT. ALL NPOES PERMITTED DISCHARGES ARE INDICATED
7.7

-------
HYLEBOS WATERWAY
Sound Refining. Three minor NPDES-permitted discharges are located on
Hylebos Waterway: Zidell Dismantling, Buffelen Woodworking, and U.S. Gyp-
sum. NPDES permit effluent discharge limits for these industries typically
do not limit the contaminants discussed in this report. The only contaminant
of concern specifically regulated through the permit limits of dischargers
is lead (at Pennwalt and Occidental Chemical Corporations). Annual monitoring
of zinc, copper, iron, and nickel are also required at Occidental Chemical
Corporation.
7.2.1.3 Dredging History--
Dredging by the Port of Tacoma and the U.S. Army Corps of Engineers
has changed the shape and size of Hylebos Waterway over the years (Figure
7.2.3). When the waterway was created in the 1920s, it extended only to
the point of what is now the lower turning basin, approximately 12,000
ft from the mouth of the waterway. Channel deepening and some shoreline
modification resulted from dredging activities in 1931, 1934, 1939, 1945,
and 1951 (Dames and Moore 1982). In 1954-1955, the Port of Tacoma extended
the waterway 3,800 ft (Johnston 1981). Subsequent dredging by the Corps
of Engineers in 1958, 1962, and 1964-1966 widened the upper waterway and
created the upper turning basin (Dames and Moore 1982). The most recent
maintenance dredging, which occurred in 1972, was confined to the upper
turning basin and three areas in the general vicinity of the 11th Street
bridge (Landau 1984). Since 1972, the only dredging in the waterway has
been performed by specific industries along the waterfront.
7.2.2 Contaminants of Concern
Locations of sediment chemistry stations in Hylebos Waterway sampled
as part of the present investigation and all historical sampling sites
are shown in Figure 7.2.4. Hylebos Waterway has been divided into six
segments. Nine contaminants or groups of contaminants are listed in Figure
7.2.1 as preliminary contaminants of concern:
Organic Compounds
Pentachlorocyclopentane isomer (Segment 5)
Polychlorinated biphenyls (PCBs) (Segments 2,4,5)
Aromatic hydrocarbons (Segments 1,2,4)
Dibenzofuran (Segment 2)
Benzyl alcohol (Segment 2)
Chlorinated hydrocarbons (Segments 2,4,5)
(i.e., ethenes, benzenes, and butadienes)
Concentrations of the substances listed above as of preliminary concern
were later determined to exceed benthic or toxicity AET (dry weight) in
their respective areas, except dibenzofuran. Concentrations of dibenzofuran
exceeded toxicity AET after normalization to percent fine-grained material
in Segment 4 (Station HY-46), Concentrations of several of these substances
exceeded AET (dry weight) 1n other areas than those listed. However, the
entire waterway distribution of these contaminants is typically considered
Metals
Arsenic (Segments 1,2)
Copper (Segments 1,2)
Lead (Segments 1,2)
Z1nc (Segments 1,2)
Mercury (Segments 2,5)
7.8

-------
Corps of Engineers Dredging
Other dredging projects
Quantity
Year
Quantity (cu. yds.)
Map #
Permittee
Year
feu. vds.)
1931
645,000

Port of Tacoma
1954-55
unk.
1931
102,000
1
Commencement Bay Marina
1981
8,000
1939
761,000
2
Donald S. Olson
1976-78
250
1945
46, 000
3
Sound Refining
1967
23,600
1951
167, 000
3
Sound Refining
1970-71
9,000
1958
17,000
3
Sound Refining
1975
95,000
1962
376,000
4
Cascade Pole
1973
1,100
1964-66
1,778,000
5
Marine Technical Services
1980
1,000
1972
109, 000
6
General Metals
1972
4,100


6
General Metals
1974-75
5,000


6
General Metals
1979
2,000


6
General Metals
1984
3,000
1W-K
500
1000
| FEET



^ METERS

0
250
500

Other dredqinq projects




Quantity
Map #
Permittee
Year
(cu. yds.)
7
Tacoma Boat Building
1976
2,500
8
Glacier Sand S Gravel
1973
600
8
Glacier Sand G Gravel
1982
3,000
9
Weyerhaeuser
1970
20,000
9
Weyerhaeuser
1970
600
9
Weyerhaeuser
1972
35,000
9
Weyerhaeuser
1972
1,500
9
Weyerhaeuser
1976
4,100
10
Pennwalt Corp.
1982
600
11
Occidental Chem. Corp.
1967-68
15,500
11
Occidental Chem. Corp.
1974
10,600
Figure 7.2.3
DREDGING ACTIVITY IN THE HYLEBOS WATERWAY
Location of Corps of Engineers dredging projects estimated
from sketches obtained from D. Kama, EPA. Only the most
recent dredging shown 1n any given area. Private dredging
activities determined by review of COE dredging.permit
applications, 1967-1984.

-------
Sediment Core
HY-63C
Sediment Core
HY-63
Sediment Core
HY-63A
Sediment -
Core HY-62
Sediment Core
HY-63B
Sediment Core
HY-61
Sediment Core
HY-60A
Sediment Core
HY-60B
~	WDOE, 1984
0	WDOE. Historical
A	EPA
O	Tetr» Tech
X	Other Agencies
800 1000
FEET
280
800
Figure 7.2.4
SURFICIAL SEDIMENT STATIONS AND SEDIMENT CORE LOCATIONS
FROM ALL HYLEBOS WATERWAY STUDIES IN THE PROJECT DATA BASE
7.10

-------
HYLEBOS WATERWAY
during source evaluations in any one area. Other contaminants with concentra-
tions that were ultimately determined to exceed AET but were not subjected
to source evaluations include:
Substance
Station Where AET (DW) Exceeded
Phenol
Phthalate esters
N-nitrosodiphenyl amine
Antimony
Nickel
HY-01,	HY-12, HY-16, HY-22, HY-36
HY-12,	HY-22
Hy-31	HY"33
HY-16,	HY-19 (and intertidal sediments)
HY-22,	HY-23 (and intertidal sediments)
Tentatively identified compounds for which concentrations also exceeded
AET but were not evaluated for sources included: 1-methyl(2-methylethyl)-
benzene, biphenyl, dibenzothiophene, methylphenanthrenes , methylpyrenes].
All of these tentatively identified compounds likely share common sources
with the PAH. These substances are not discussed further.
The simplified distribution of each preliminary contaminant of concern
in the surficial sediments of Hylebos Waterway is presented in Figure 7.2.5.
Distributions are based on data from Tetra Tech sampling events and all
historical studies. Compounds elevated above the bay-wide 90th percentile
concentration that have not been designated as preliminary contaminants
of concern are also shown in Figure 7.2.5. For example, copper concentrations
are elevated above the 90th percentile in Segment 5, but copper is not
a contaminant of concern in Segment 5. Copper is a contaminant of concern
in Segments 1 and 2 and is elevated above the 90th percentile in those
segments. Figure 7.2.5 is presented to show the most contaminated areas
of the waterway and to show parallels among the distributions of the contam-
inants, since contaminants with similar distributions may have common sources.
The areas of elevated contaminant concentrations are Indicated by lines.
The fine lines Indicate areas 1n which the concentration of the contaminant
exceeded the 80th percentile of that contaminant's concentrations 1n all
Tetra Tech stations or August, 1984, Port of Tacoma stations throughout
the nearshore/tideflats study area. The heavy lines Indicate areas that
exceeded the 90th percentile of the concentrations in samples from these
stations. Areas of high concentration may not coincide with areas of concern
for each contaminant, since the latter reflects biological as well as chemical
data.
Four trends are apparent from Figure 7.2.5:
•	Hylebos Waterway Segments 2 and 5 had the greatest number
of contaminants with concentrations exceeding the 80th and
90th percentile.
•	The sediments near the mouth of the waterway (Segment 6)
were relatively uncontaminated.
7.11

-------
PCB
LOW MOLECULAR WT. PAH
HIGH MOLECULAR WT. PAH
DIBENZOFURAN
BENZYL ALCOHOL
TOTAL CHLOR. BUTADIENES
TETRACHLOROETHENE
PENTACHLOROCYCLOPENTANE
ARSENIC
COPPER
LEAD
ZINC
MERCURY
CMtMriMfit Concentrations
Exceed 0Oth Percentile
I ContMrtnwit Concentrations
Exceed 90th Percentile
HEXACHLOROBENZENE ! -
Segment
Segment
Segment 4
Segment 3
Segment 2
Segment 1
Figure 7.2.5
AREAS OF HYLEBOS WATERWAY WITH THE
GREATEST CONCENTRATIONS OF EACH CONTAMINANT
OF CONCERN IN THE SURFICIAL SEDIMENTS

-------
HYLEBOS WATERWAY
•	Segment 5 was characterized by elevated concentrations of
most of the identified chlorinated organic compounds (hexa-
chlorobenzene, chlorinated butadienes, a pentachlorocyclopentane
isomer, tetrachloroethene, and PCBs).
•	Since a similar pattern of contamination was seen for hexachloro-
benzene, the chlorinated butadienes, and the pentachlorocyclo-
pentane isomer, common sources may be responsible. Amass
of unidentified chlorinated compounds is characteristic
of Hylebos Waterway; the reported compounds represent only
a small fraction of this class of compounds.
Average mass flux estimates were calculated for chlorinated benzenes,
chlorinated butadienes, chlorinated ethenes, arsenic, copper, lead, and
zinc to enable a comparison of mass loadings of these contaminants relative
to their sediment concentrations in Hylebos Waterway. Insufficient source
data were available to calculate mass flux estimates for the other priority
contaminants. The mass flux estimates were evaluated using average concentra-
tions of the contaminants in sediments from all present and historical
stations according to the procedures and criteria outlined in Section 2.12.3.2.
All of the source-derived mass fluxes were within an order of magnitude
of the concentration-derived mass fluxes with the exception of chlorinated
benzenes and chlorinated ethenes. Therefore, according to the uncertainty
criteria for this analysis, no data gaps were indicated in accounting for
major sources of chlorinated butadienes, arsenic, copper, lead, or zinc.
The source-derived mass flux for chlorinated ethenes and benzenes was less
than 0.1 to 1 percent of the concentration-derived mass flux. A data gap
in the identification of sources of these chlorinated compounds is indicated.
In the following sections, each contaminant (or contaminant group)
of concern is addressed individually. Its spatial distribution within
the waterway sediments is discussed, contaminant loadings from known sources
are calculated, and all known or potential sources are evaluated.
7.2.3 Polychlorinated Biphenyls
7.2.3.1 Spatial Distribution--
PCB concentrations were highly variable 1n Hylebos Waterway sediments.
(Figure 7.2.6). Concentrations were consistently below 200 ug/kg 1n Segment
1 at the head of the waterway. Maximum PCB concentrations exceeded 1,000
ug/kg in all other segments. This patchy distribution remained after
concentrations were normalized to organic carbon, suggesting that PCBs
in Hylebos Waterway do not come from the major carbon sources 1n the waterway
(e.g., Kaiser Ditch, silt from the Puyallup River; see Section 3.1.1.3),
but from multiple local sources.
The highest PCB concentrations (dry weight) 1n Hylebos Waterway Segment
5 were restricted to the southern shore of the waterway (Figure 7.Z.7).
With increasing distance from shore, PCB concentrations dropped off abruptly.
The same pattern was evident when concentrations were normalized to total
7.13

-------
Segment
r.
ZT>
*C>
*
*D
.O
a
r tn
c
») o
t> <0
3 3
M
iw
¦D
t>
(0
U
c
0
o
Benthlc
Effects
AET
T
6 8 10 i:
(Thousand*)
Ft. from mouth of waterway
Segment 6
o
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60 -
50 -
40 -
30 -
20
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+ +0°D
>| ft -
-------
Cone, in sed. — ppm dry weight
-N-
.28
V*1.1
*1.1
0.04
U0.1 110.07
#1.1
0.11
U0.1
:o 2
*.75 ~
U0.01
~ Tetra Tech Survey Data
A EPA Data
x Data From Other Agencies
* Exceeds AET
(see Table 4.2 for AET values)
Figure 7.2.7
CONCENTRATIONS OF TOTAL PCBs IN THE SURFICIAL SEDIMENTS
OF THE HYLEBOS WATERWAY SEGMENT 5
U = undetected with the detection limit shown
-------
HYLEBOS WATERWAY
organic carbon content. The extent of the contaminated zone along the
length of the waterway cannot be clearly defined because of the absence
of data to the west of Station HY-46 (280 ug/kg). However, the contamination
extended at least 1,500 ft along the waterfront. The spatial gradient
indicates that the source of PCB contamination is along the southern shore
of the waterway.
PCB concentrations in sediment cores from Hylebos Waterway Segment
5 (Figure 7.2.8) peaked at depth in the sediment colunn. (Four core samples
were taken in this area, but only two are shown. PCB detection limits
for the other two cores exceeded 1,000 ug/kg for several of the horizons.)
Although the depth of the subsurface maximum varied among samples, the
contamination extended to at least 0.4 m depth. At core Stations HY-63-B
and HY-63-C, decreasing concentrations in the upper horizons indicate that
resent levels of contaminant input are less than they had been. It should
e noted, however, that PCB concentrations throughout these cores were
well below the surficial sediment concentrations at other stations within
Segment 5. Core samples were composited over large intervals, possibly
masking bands of high PCB contamination and precluding a conclusion about
whether contamination is ongoing, historical, or both.
PCB distribution in surficial sediments of Hylebos Waterway Segments
2 and 3 is shown in Figure 7.2.9. The highest concentration of PCBs was
2,000 ug/kg (Segment 2, Station HY-22). This same station is identified
elsewhere in this report as a site of anomalously high concentrations of
chlorinated hydrocarbons, polycyclic aromatic hydrocarbons (PAH), and dibenzo-
furan. The high concentrations of these compounds and PCBs at this station
may be a consequence of 1982 dredging by Pennwalt Corporation that exposed
buried contaninated sediments. Less than 100 ug/kg PCB was found in surficial
sediment samples (High 1982) just prior to the dredging.
Further evidence that the high PCB concentrations resulted from exposure
of buried sediments is provided by a sediment core sample taken 150 m northwest
of Station HY-22 prior to the 1982 dredging (Riley 1981, Station 3). PCB
concentrations in this core (Figure 7.2.10, top) increased with depth down
to at least 0.35 m in the sediment. The highest PCB concentration observed
in these buried sediments (2,500 ug/kg) corresponded closely to that observed
in the surficial sediments at Station HY-22 (2,000 ug/kg). This suggests
that lower PCB-contaminated horizons noted in Riley's (1981) core are now
exposed on the surface at Station HY-22 as a result of the recent dredging
and that the contamination is principally historical.
A relatively high PCB concentration (1 ,500 ug/kg) was also apparent
1n the central portion of the waterway at Station HY-23, 12,000 ft from
the mouth. The 1982 Pennwalt dredging was restricted to within 40 m of
the shoreline and therefore would not have affected PCB concentrations
at Station HY-23. The reason for the elevated PCB levels at HY-23 is unknown.
Possible explanations include ship scour or release from adjacent dredging
operations.
7.16
-------
(A)
Concentration (yg/kg dry weight)'
10
1 '
100
jlJ
i I
1,000
¦ . '
0.2 -
0.4 ¦
(B)
Concentration (yg/kg dry weight)3
10 100 1,000

0.4
Figure 7.2.8
CONCENTRATIONS OF TOTAL PCBs WITH DEPTH IN THE SEDIMENT COLUMN
(Station locations are shown in Figure 7.2.4)
(A) STATION HY-63B.B03
(B) STATION HY-63C.B05
No AET exceeded in these cores
(see Table 4.2 for AET values)
7.17
-------
110
-N-
1100
L95
26
190
!50 Wl?
JA3»0 X
~isoon*530*
S#2QOO 200
>P ~ X
/\ 330
\ 270
v\
210
& [PA diU
+ WOE, 1984 datt
* D*U frtw other cjcncles
~ Exceeds AET
(see Table 4.2 for AET values}
Figure 7.2.9
CONCENTRATIONS OF TOTAL PCBs IN THE SURFICIAL SEDIMENTS
OF HYLEBOS WATERWAY SEGMENTS 2 AND 3
(pg/kg dry weight)
L = At least one of the components of the
group was undetected; sum includes
the detection limit.
7.18
-------
(A)
10
a>
E
"S o,
«/>
Q.
-------
HYLEBOS WATERWAY
PCB concentrations were also high (860-1,100 ug/kg) in sediments from
Hylebos Waterway Segment 3 near the Lincoln Avenue drain (HY-066) and drains
HY-062 and HY-061 (Figure 7.2.9). These drains do not appear to be potential
recent sources, as shown by the low level of contamination in other stations
near the drains. Therefore, the distribution of PCBs in this segment is
patchy, as in other waterway areas, and the sources are undetermined.
7.2.3.2 Loading Estimates--
The only discharge to Hylebos Waterway documented to contain PCBs
is Kaiser Ditch (HK-052). One effluent sample from this ditch contained
less than 2 ug/L PCB (WDOE unpublished). No PCBs were found in nine other
analyses of the discharge (detection limits 0.1-2 ug/kg for individual
Aroclor mixtures). All other discharges to Hylebos Waterway in which PCBs
have been undetected are listed in Table 7.2.1.
7.2.3.3 Source Identification--
A1 though there are several potential sources of PCBs, both historical
and possibly ongoing, sediment data and the available loading data do not
allow confirmation of either historical or ongoing sources.
7.2.3.4 Summary and Recommendations--
In both lower Hylebos Waterway (Segment 5) and upper Hylebos Waterway
(Segments 2 and 3), the spatial patterns of PCB contamination were highly
variable. This distribution suggests that there are no major contributions
by ongoing sources. In lower Hylebos Waterway, PCB concentrations were
elevated along the length of the Occidental Chemical Corporation waterfront.
In upper Hylebos Waterway, sediment PCB concentrations were elevated 1n
several areas, including a site adjacent to the Pennwalt Corporation's
dock and main outfall. This elevation may have resulted from the recent
exposure of buried sediments.
It 1s unknown 1n most areas whether high PCB levels 1n Hylebos Waterway
sediments result from ongoing or historical sources. The highly variable
PCB levels 1n surficial sediments may result from exposure of historically
contaminated sediments (e.g., from ship scour or dredging) or from transport
and deposition of contaminated sediments within the waterway. Several
industrial activities (e.g., transformer Installations) on Hylebos Waterway
could be ongoing sources of PCBs. However, the composition of PCBs within
waterway sediments 1s not characteristic of unweathered PCBs from transformers.
PCB concentrations in Hylebos Waterway did not correlate with those of
any other contaminant for which a potential source has been Identified.
Commercial PCB mixtures are often significantly altered by physlcochemical
and biological processes after they are released into the terrestrial or
marine environment. Sedimentary PCB assemblages commonly reflect alterations
that have occurred during environmental transport as well as alterations
that have occurred after deposition 1n the sediments. Anong the most important
environmental processes that modify PCB mixtures are oxidative microbial
7.20
-------
Table 7.2.1
DISCHARGES TO THE HYLEBOS WATERWAY IN WHICH PCBs HAVE BEEN UNDETECTED
Drain #
Name
No. of
Analyses
Detection Limit
(ug/L for
Individual
Aroclor Mixtures)
HC-000
Hylebos Creek
4
0.1-2
HM-028
Morningside Ditch
5
0.1-2
HY-021
30" concrete pipe
1
0.1
HY-023
18" concrete pipe
1
0.1
HY-040
8" concrete pipe
1
1-2
HY-054
East Channel Ditch
2
0.1-2
HY-056
6" concrete pipe
1
0.1
HY-058
Main Pennwalt outfall
1
unspecified
HY-066
Lincoln Avenue Drain
3
0.1-2
HY-076
30" concrete pipe
1
0.1
HY-078
12" concrete pipe
3
0.5-2
HY-083
2 seeps at Occidental
2
0.5-2
HY-085
7 steel pipes
2
0.05-2
HY-700
Pennwalt East Seep
3
0.05-2
HY-707
Main Occidental outfall
5
1
HY-709
Pennwalt sewer pipe
1
0.1
7.21
-------
HYLEBOS WATERWAY
degradation (which tends to preferentially affect less chlorinated PCB
congeners), the loss of more water soluble (less chlorinated) congeners
to an aqueous phase, and the loss of more volatile (less chlorinated) congeners
to a vapor phase. As a net result of one or more of these processes, sedi-
mentary PCB mixtures are often enriched in more highly chlorinated congeners
relative to the commercial mixtures from which they derived. Therefore,
the observation that PCB mixtures in Hylebos sediments appear to be weathered
does not imply that the deposits are historical only. The weathering processes
may occur on land (e.g., in a landfill) with subsequent transport to and
ongoing contamination of the waterways.
A general survey of possible upland PCB sources should be conducted
in areas adjacent to Hylebos Waterway, particularly in areas near potential
sources (e.g., transformer installations). Additional data on the vertical
distribution of PCBs in Hylebos Waterway sediments should be collected.
Future dredging activities in Hylebos Waterway should minimize exposure
of deeper sediments that may be contaminated by PCBs.
7.2.4 Aromatic Hydrocarbons
7.2.4.1 Spatial Distribution--
Both low and high molecular weight polycyclic aromatic hydrocarbons
(LPAH and HPAH) have been identified as preliminary contaminants of concern
in Hylebos Waterway within Segments 1, 2, and 4. Surficial sediment concentra-
tions of LPAH ranged from 237 to 52,000 ug/kg with most sediments below
3,000 ug/kg (Figure 7.2.11). The highest concentrations occurred in three
areas. The maximum value for LPAH was observed off the Kaiser Ditch in
Segment 1. Concentrations dropped from 52,000 ug/kg at the ditch to 3,700
ug/kg dry weight at the nearest Tetra Tech sampling station (HY-16). A
second peak was located near 12,000-14,000 ft from the waterway mouth (Hylebos
Waterway Segment 2), along the south shoreline and in the central channel
(Figure 7.2.12). As noted earlier, the sediments nearest the southern
shoreline in this area (Station HY-22, 4,400 ug/kg LPAH) may have been
disturbed by recent dredging.
The third peak was within a broad area between 3,000 and 7,000 ft
from the waterway mouth (Segments 4 and 5). From a two-dimensional plane
view (Figure 7.2.12), concentrations 1n this region were elevated relative
to those in other areas, but there was no consistent spatial gradient of
contamination within the area itself. LPAH concentrations were elevated
in numerous Isolated stations (e.g., 9,500 ug/kg at a 1984 WD0E station
on the south shore by Drain HY-078, and 12,000 ug/kg near the Naval Reserve
Dock), suggesting multiple sources rather than a dominant point source.
High LPAH concentrations were also found at a single staton (HY-16)
at 14,000 ft from the mouth of the waterway, immediately off the Kaiser
Ditch outfall. At two stations from historical studies, anomalously high
concentrations for LPAH were found. These stations (the Naval Reserve
dock, at 5,000 ft from the mouth, and drain HY-078, at 6,900 ft from the
mouth) are discussed 1n Section 7.2.4.3 (Source Identification).
7.22
-------
Segment
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0 Tetra Tech Investigation - quantltated value
~ Other Investigations - quantltated value
a Tetra Tcch Investigations - less than value
~ Other Investigations - lets than value
1 Other Investigations - undetected value
Figure 7.2.11
T—
12
"T
1 qD
5 oq
14
16
(A)
Benthlc effects
and toxicity
AET
Benthlc effects
AET
not exceeded
Toxicity
AET
(B)
CONCENTRATIONS OF TOTAL LOW MOLECULAR WEIGHT POLYCYCLIC AROMATIC HYDROCARBONS
IN THE SURFICIAL SEDIMENTS OF THE HYLEBOS WATERWAY WITH DISTANCE
FROM THE MOUTH OF THE WATERWAY
(A) Concentrations on a dry weight basis
(8) Concentrations normalized to total organic
carbon content of the sediments
7.23
-------

s*
~ WDOE, 1964
0 W>OE. Historical
A EPA
~ Tctr* Ttch
X Other Agencies
meters
Figure 7.2.12
SURFICIAL SEDIMENT CONCENTRATIONS OF LPAH IN HYLEBOS WATERWAY
L = At least one of the components of the group was undetected,
sum included the detection limit.
Z = Data corrected for blank.
U = Indicates undetected at value shown.
7.24
-------
HYLEBOS WATERWAY
Patterns of HPAH concentrations in surficial sediments of Hylebos
Waterway (Figures 7.2.13, 7.2.14) were quite different from those of LPAH.
Concentrations of HPAH peaked dramatically at 14,000 ft from the mouth
of the waterway (Segment 1) , decreasing towards both the head and mouth
of the waterway. When normalized to the total organic carbon content of
the sediments, there was only a slight decrease in the average HPAH concen-
tration in sediments near the mouth of the waterway compared to those near
the head (Figure 7.2.13). Therefore, the substantial HPAH concentrations
observed on a dry-weight basis appear to be associated with an accumulation
of HPAH- contaminated organic material in the sediment. It is likely that
a major organic carbon source in the vicinity of 14,000 ft from the mouth
of Hylebos Waterway is also the major HPAH source. Maximum HPAH concentrations
occur on the south shore at the Kaiser Ditch (370,000 ug/kg dry weight,
Figure 7.2.14).
The two- and three-ring PAH that constitute the LPAH group are most
abundant in uncombusted fossil fuels such as petroleum, oil shales, and
their refined products. The four- to six-ring PAH that constitute HPAH
group are generated by combustion of wood and fossil fuels (Lee et al.
1977). Thus, a comparison of the relative abundances of LPAH and HPAH
in the environment may sometimes indicate whether the predominant source
is the combusted fuels or uncombusted fossil hydrocarbons. The HPAH-to-LPAH
ratio for sediments of Hylebos Waterway increased from the mouth of the
waterway (ratio of approximately 2) to the head (ratio of approximately
11; Figure 7.2.15). This provides strong evidence that the sources of
PAH to upper Hylebos Waterway are very different from those to lower Hylebos
Waterway. The PAH in upper Hylebos Waterway are derived primarily from
combustion. Those in lower Hylebos Waterway are derived relatively more
from unburned fossil fuels.
The vertical pattern of PAH contamination in sediments was consistent
throughout Hylebos Waterway (Figure 7.2.16). Generally, sediment core
samples from the mouth of the waterway (HY-63), midway along its length
(HY-61) and at the head (HY-60A) had greater concentrations of LPAH and
HPAH in subsurface horizons relative to the less contaminated upper horizons
with the exception of HPAH in HY-63). This pattern has been observed
n other sediments within central Puget Sound (Crecllius and Bloom in review;
Barrick and Prahl in review). Concentrations of the LPAH in each of the
cores exceeded benthic and toxicity AET at depth. HPAH concentrations
at depth were well above AET toward the head of the waterway.
7.2.4.2 Loading Estimates--
Despite sampling of numerous discharges to Hylebos Waterway, few samples
have been found to contain PAH, given the techniques and detection limits
used (typically <10 ug/L). Kaiser Ditch (HK-052) 1s the only discharge
that has consistently been found to contain PAH, and for which loading
estimates are available. Based on 11 observations from June, 1980 to April,
1984, estimated loading 1s less than 0.046 lb/day LPAH, based on an average
concentration of less than 3.2 ug/L (WD0E unpublished). Phenanthrene was
7.25
-------
X
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Benthic
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AET
Toxicity
AET
6 8 10 12
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Ft. from mouth of waterway
14
16
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Segment
1.9
1.6
1.7
1.6
1.5
1.4
1.3
1.2
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(B)
1 1 i 1 1 1 r
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(Thousands)
Ft. from mouth of watsrwoy
OTetra Tech Investigation - qvantltated value
© other Investigations - qvantltated value
* Tetra Tech Investigations - less thin value
v Other Investigations - less than value
* Other Investigations - undetected value
Figure 7.2.13
CONCENTRATIONS OF TOTAL HIGH MOLECULAR WEIGHT POLYCYCLIC AROMATIC HYDROCARBONS
IN THE SURFICIAL SEDIMENTS OF THE HYLEBOS WATERWAY WITH
DISTANCE FROM THE MOUTH OF THE WATERWAY
(A) Concentrations on a dry weight basis
(B) Concentrations normalized to total organic
carbon content of the sediments
7.26
-------
L2.0
~ l.l
~5.9
24.1
.3.9
Z4.6
5.0
L12.
6.»
7.4
~19.
18.
7.9
.24.
~ 22.
~ 17
~ NDOEi 1964
0 WDOE, Historical
A EPA
~ Tetre Tech
X Other Agencies
16.
800 1000
FEET
6.6
METERS
L7.8
250
800
Figure 7.2.14
SURFICIAL SEDIMENT CONCENTRATIONS OF HPAH IN HYLEBOS WATERWAY
L = At least one of the components of the group was undetected,
sum included the detection limit.
Z = Data collected for blank.
7.27
-------
5.3
~4.6
~4.8
~3.5
2.9 Q ~ 2.8
41 2.2 a 3.4n^
v? °2-4
~2.5
~ 2.8
~ 1.9
~1.8
~ 11.0
7.2D
7.9
la6liii n ^ n"7
D 11*0 i—» D
r*-3
~15.9
~ 6.8
1000
¦3 FEET
500
METERS
500
250
Figure 7.2.15
RATIO OF THE CONCENTRATIONS OF TOTAL HIGH MOLECULAR WEIGHT PAH
TO TOTAL LOW MOLECULAR WEIGHT PAH AT ALL TETRA TECH
SURVEY STATIONS IN THE HYLEBOS WATERWAY
-------
1,000
Concentration (pg/kg dry weight)
10,000
TT
i l
I
100,000
—I—l_i
LPAH
Benthic effects —
and toxicity AET
1,000
1,000
m
T

HPAH
Toxicity AET
Benthic effects AET
(A)
I
10,000
I
I
10,000
100,000
I I I I
(B)
n
11
100,000
(C)
!I
! I
i_L
Figure 7.2.16
CONCENTRATIONS OF PAH WITH DEPTH IN THE SEDIMENT COLUMN
(A) STATION HY-63, G01; (B) STATION HY-61, B02;
(C) STATION HY-60A, B01
Low molecular weight PAH
High Molecular weight PAH
7.29
-------
HYLEBOS WATERWAY
the LPAH detected most consistently in the samples. Estimated loading
of HPAH during the same period is less than 0.15 lb/day, based on an average
concentration of less than 10.4 ug/L. The HPAH compounds consistently
detected include pyrene, fluoranthene, chrysene, and benzofluoranthenes.
The PAH loading from deposition of stack emissions from Kaiser Aluminum
have not been quanitifed. However, most of the PAH deposited within the
study are probably enter Commencement Bay via surface water runoff because
of the more extensive surface area for atmospheric fallout on land compared
with direct deposition in the waterways.
PAH have also been detected in Morningside Ditch (HM-028), the East
Channel Ditch (HY-054), a seep at U.S. Gypsum (HY-061), a drain near Buffelen
Woodworking (HY-070), drains near Occidental Chemical Corporation (HY-085),
and storm sewer and groundwater seeps along the Pennwalt Corporation shoreline
(HY-056, HY-700, HY-701). However, because of low concentrations, infrequency
of detection, and low estimated loadings, these discharges are not considered
to be major sources of PAH to the waterway. Discharges that did not contain
PAH are listed in Table 7.2.2. Insufficient data are available to make
a reliable determination of the mass flux of PAH in Hylebos Waterway.
7.2.4.3 Source Identification--
The spatial gradients of contamination in Hylebos Waterway indicate
two areas of elevated LPAH concentrations: 12,000 ft from the mouth (Segment
2) and 3,000 to 7 ,000 ft from the mouth (Segments 4 and 5). In addition,
a source of HPAH was noted 14,000 ft from the waterway mouth (Segment 1).
These three areas are discussed individually below.
Hylebos Waterway Segment 2-- The highest level of LPAH contamination
(on a dry-weight basis) found 1n Hylebos Waterway during the Tetra Tech
survey was observed at 12,000 ft from the waterway mouth, immediately adjacent
to the Pennwalt dock and discharge point of the plant effluent. No LPAH
have been found in the Pennwalt effluent above trace amounts (Yake 1982a,
detection limits unspecified). However, one or more petroleum spills may
have occurred at the dock. Fuel oil for plant consumption is received
at the dock and piped to three storage tanks with a total 27,000-barrel
capacity (U.S. Army C0E 1983). A thorough search of WD0E files on Pennwalt
Corporation and a review of recent WD0E Environmental Complaint files (1979-
1985) uncovered only a single spill of petroleum on the Pennwalt property.
On February 9, 1982, 200-300 gal of Bunker C oil were spilled, although
less than 1 gal was estimated to have reached the waterway. Spills of
sufficient volume to account for observed contamination of waterway sediments
cannot be documented.
The relative proportion of alkylated LPAH was investigated to help
determine the origin of the PAH 1n the sediments. PAH mixtures 1n uncombusted
fossil fuels typically contain relatively more alkylated PAH than do combustion-
derived PAH, which primarily contain only the nonalkylated analogs (Youngblood
and Blumer 1975). Thus the ratio of 2-methyl phenanthrene to phenanthrene
from a source of combustion-derived PAH can be expected to be relatively
7.30
-------
Table 7.2.2
DISCHARGES TO THE HYLEBOS WATERWAY IN WHICH PAH HAVE BEEN UNDETECTED
Detection Limit
(ug/l for
No. of Individual
Drain #
Name
Analyses
Aroclor Mixtures)
HC-000
Hylebos Creek
5
0.1-10
HY-016
Crack 1n Bulkhead
1
0.5
HY-017
12" corrugated pipe
1
unspecified
HY-0I8
8" steel pipe
1
0.5-50
HY-021
30" concrete pipe
1
10
HY-023
18" concrete pipe
1
10
HY-040
8" concrete pipe
1
0.1-1
HY-058
Pennwalt main outfall
2
unspecified
HY-062
12" concrete pipe
1
0.5
HY-066
36" concrete pipe
3
0.1-10
HY-070
Flow over bulkhead
1
0.5
HY-071
6" and 12" iron pipes
1
unspecified
HY-073
Open channel
1
0.5
HY-076
30" concrete pipe
1
10
HY-078
12" concrete pipe
2
0.1-1
HY-083
2 seeps at Occidental
2
0.1-1
HY-704
Sound Refining main outfall
2
unspecified
HY-707
Occidental main outfall
5
10
HY-709
Pennwalt sewer pipe
2
1
7.31
-------
HYLEBOS WATERWAY
low. Uncombusted PAH, as would be involved in a spill, can be expected
to have a higher 2-methyl phenanthrene-to-phenanthrene ratio. This ratio
was calculated for all Tetra Tech stations in Hylebos Waterway and showed
extreme variation (0.056-0.63) with no apparent gradient. The sample immedi-
ately adjacent to the Pennwalt dock (Station HY-22) had the highest ratio
(0.63) of all stations, but there were no samples where methylated phenanthrenes
were found in higher concentration than phenanthrene as is often found
in fuel oils. If spills have occurred, there has probably been considerable
degradation of the oils.
As noted earlier, Pennwalt Corporation dredged an area immediately
adjacent to the plant dock in 1982. Station HY-22 was within this area
and, therefore, the sample probably represented deeper sediments exposed
by recent dredging. The sediment cores indicate that PAH concentrations
in subsurface sediments were typically greater than those of surface sediments.
Therefore, the high PAH concentrations at Station HY-22 are probably not
a consequence of proximity to a source, but instead, result from sampling
buried, contaminated sediments exposed by the recent dredging.
Elevated LPAH concentrations (3,300-3,900 ug/kg) noted in the central
waterway off the Pennwalt Corporation cannot be explained. No source has
been identified for the contamination in the central waterway.
Hylebos Waterway Segments 4 and 5--Sediments from a broad area of
lower Hylebos Waterway (3,000 to 7,000 ft from the mouth) had elevated
concentrations of LPAH. Within this area, there were two stations with
extremely high LPAH concentrations (at 5,000 ft and 6,900 ft from the mouth).
The station at 5,000 ft is off of the Naval Reserve dock, a facility known
to have discharged petroleum products. Concentrations at other stations
in this area were much lower. Indicating that the area of elevation is
relatively small. The station at 6,900 ft 1s off of drain HY-078. Concentra-
tions at other stations in this area also were much lower, indicating that
the area of elevation 1s relatively small. Samples from drain HY-078 and
neighboring drain HY-076 have been analyzed for LPAH (HY-078 twice and
HY-076 once) and none were detected. Periodic releases from these drains
are possible. These generally lower elevations are considered to indicate
multiple sources rather than a dominant point source.
In the absence of a clear spatial gradient or documented discharge
of PAH, it is impossible to definitively Identify the ultimate sources.
Such a conclusion is not surprising for a heavily industrialized waterway
such as Hylebos Waterway. Because of ubiquity of fossil fuels and their
combustion products, virtually every ship traveling the waterway and every
industry along its banks is a potential source of PAH.
Any one of the Industries surrounding Hylebos Waterway Segments 4
and 5 could be a potential source of LPAH (Table 7.2.3). None can be shown
to be responsible for the observed contamination of Hylebos Waterway sediments.
However, Sound Refining, PRI Northwest, and Cenex may be potential sources
because oil and gasoline spills have been docimented at these facilities.
Source identification efforts are hindered by (1) apparent absence of spatial
7.32
-------
Table 7.2.3
POTENTIAL INDUSTRIAL SOURCES OF POLYCYCLIC AROMATIC HYDROCARBONS
IN HYLEBOS SEGMENTS 4 AND 5
Facility Name
Sound Refining
PRI Northwest (pro-
perty formerly owned
by Fletcher Oil)
Cenex (formerly
Western Farmers)
Occidental Chemical
Corporation
Tacoma Public
Utilities, Steam
Plant No. 2
Association with PAH
Petroleum refinery; loading/unloading
of petroleum products at wharf; fuel
storage and distribution
Petroleum distributor; receipt of pro-
ducts by ship for overland distribu-
tion
Fuel tanks for trucks and equipment
Receipt of fuel oil by ship for plant
consumption
Inactive steam plant; dock formerly
used for receipt of fuel oil for plant
consumption
Known Problems
Past leakage of oil/water mixture
from lines leading to oil/water
separator®
69-gallon unleaded gas spill, 7/l/79b
50-gallon gasoline spill, 3/17/80";
Floor of tank farm and surrounding
berms built from dredge spoil; ground
water contamination possible0
200 to 300-gallon gasoline spill,
1/11/79, estimated 30 gallons reached
the waterway''
None
None
aR. Robinson, Tacoma Sewer Utilities, pers. comm.
^WDOE Environmental Complaint Files
CJ. Oberlander, WDOE, pers. comm.
-------
HYLEBOS WATERWAY
gradients of contamination, (2) absence of documented discharges of appreciable
quantities of PAH, and (3) numerous potential contaminant sources.
Hylebos Segment 1--The high HPAH concentrations noted in sediments
of upper Hylebos Waterway at about 14,000 ft from the mouth of the waterway
corresponded to the location of the Kaiser Ditch discharge. A single sample
with high LPAH concentrations (3,680 ug/kg) was collected near the same
outfall. Discharge from the ditch has consistently had detectable quantities
of LPAH and HPAH. The following discussion is focused on HPAH, since the
spatial gradients of contamination and loading information indicate that
the ditch is a much greater source of HPAH than of LPAH.
There are two principal sources of HPAH to Kaiser Ditch: atmospheric
emissions and wet scrubber sludges from Kaiser Aluminum and Chemical Corpora-
tion. Atmospheric emissions from Kaiser Aluminun and Chemical Corporation
may enter Kaiser Ditch via direct deposition or via runoff from areas where
particulate emissions have been deposited on the ground. Though very little
data are available to quantify HPAH loading from this source, the limited
data that do exist suggest that release of HPAH from atmospheric emissions
at Kaiser are and have been significant. Each Soderberg cell at Kaiser
has a hood that is vented to a baghouse. Potroom roof monitors, which
receive only contaminants that escape the hoods, were releasing 0.67 lb/day
benzo(a)pyrene in 1984 (Fenske 1985). The benzo(a)pyrene loading from
total atmospheric emissions at Kaiser may be much greater. There has been
no known attempt to quantify HPAH loading from the baghouses. Particulate
material settling on Kaiser's potroom roofs contains 1.1 percent PAH (Nord
1983), thus providing additional evidence that atmospheric emissions from
Kaiser Aluminum and Chemical Corporation may represent a significant source
of PAH.
It is not possible to quantify the PAH loading from atmospheric emissions,
either by direct deposition in the waterway or via runoff. However, given
the relative land and water surface areas, it is reasonable to assume that
most of the HPAH entering Hylebos Waterway that originated from atmospheric
sources at Kaiser would first be deposited on land, then enter Kaiser Ditch
or other surface water drains, and eventually discharge into Hylebos Waterway
via runoff.
Wet scrubber sludges represent a second source of HPAH to Kaiser Ditch.
In an effort to reduce atmospheric emissions from the aluminum smelting
process, Kaiser Aluminum and Chemical Corporation operated a wet scrubbing
system from 1964 to 1974. The wet scrubbing generated a sludge containing
aluminum, reduction cell bath materials, carbon, and condensed pitch volatiles
(Hanneman 1984). This sludge was discharged Initially to a settling pond
and was later moved to two nearby diked disposal areas 1n the western portion
of the plant property (Landau 1984). Generation of sludge ceased 1n 1974
when the wet scrubber system was replaced with a dry scrubber that recirculates
particulate material. In 1983 1t was discovered that the wet scrubber
sludges on the plant property contained up to five percent PAH and could
be classified by Washington State regulations as an "extremely hazardous
7.34
-------
HYLEBOS WATERWAY
waste" on the basis of both bioassay and PAH analyses (Stanley 1983; Landau
1984).
Sampling of Kaiser Ditch, which is adjacent to the sludge disposal
areas and ultimately discharges to Hylebos Waterway, indicated that ditch
sediments were contaminated with up to 300,000 ug/kg PAH (Landau 1984).
A recent survey of Hylebos Waterway sediments near the outfall of Kaiser
Ditch found high concentrations of PAH attributable to Kaiser but concluded
(Landau 1984)
t Release of PAH from Kaiser Aluminum and Chemical Corporation
occurred principally during dredging of the wet scrubber
settling ponds in 1969 and 1971.
• PAH-contaminated sediments (concentrations >500 ug/kg dry
weight) attributable to the firm are buried beneath relatively
uncontaminated sediments of recent deposition.
• There is no evidence of contemporary deposition of PAH from
Kaiser Aluninum and Chemical Corporation, based on the absence
of PAH in the upper sediments at concentrations above "back-
ground" levels and the absence of the Kaiser sludge chemical
"fingerprint" in surficial sediments.
The present investigation provided much additional data with which
to reassess Landau's (1984) conclusions:
• The "background" concentrations referred to by Landau (1984)
are still much higher than Puget Sound reference areas.
PAH concentrations in the surface sediments near the ditch
exceeded AET determined in this study.
• As shown by the sediment core data, contamination by HPAH
was considerably worse historically than at present.
• As shown by the spatial pattern of contamination, Kaiser
Ditch appears to be the source of the HPAH in surficial
sediments of upper Hylebos Waterway.
t As indicated by loading estimates, the ditch was a source
of LPAH and HPAH in 1983-1984, although concentrations may
have been considerably less than they had been historically
(e.g., during hydraulic dredging of the sludge settling
pond).
7.2.4.4 Summary and Recommendations--
Three areas of Hylebos Waterway were found to contain elevated concentra-
tions of PAH. In lower Hylebos Waterway (Segments 4 and 5), no source
could be definitively Identified because of the absence of clear spatial
gradients of sediment contamination, the lack of documented discharges
7.35
-------
HYLEBOS WATERWAY
of appreciable quantities of PAH, and the number of potential sources.
Contamination is believed to be a consequence of multiple sources. Small
areas of relatively high LPAH concentrations were observed near the Naval
Reserve dock and a drain (HY-078) near the 11th Street bridge.
In Segment 2, elevated PAH concentrations in sediments off the Pennwalt
Corporation dock (Station HY-22) probably reflect historical contamination
exposed by recent dredging. No source could be identified for the LPAH
contamination in the central waterway.
The largest single source of HPAH to Hylebos Waterway appears to be
Kaiser Aluminum and Chemical Corporation via discharge through Kaiser Ditch.
The firm's contribution to contamination of Hylebos Waterway sediments
is based on:
• High concentrations of HPAH in sediments immediately off
Kaiser Ditch, in comparison to relatively low concentrations
elsewhere in Hylebos Waterway
• Similarity of HPAH composition between selected Hylebos
Waterway sediments and Kaiser Aluminum and Chemical Corporation
sludge samples
• On-site disposal of sludges containing up to 5 percent PAH
• Known discharges from the sludge pits into Kaiser Ditch
as a result of surface water runoff, hydraulic dredging,
and the historical discharge of plant wastewater into the
sludge ponds
• Contamination of Kaiser Ditch sediments with up to 300,000 ug/kg
PAH
• Consistent detection of PAH in discharge from Kaiser Ditch
• Documentation of atmospheric release and deposition of PAH
at Kaiser A1urninun and Chemical Corporation.
Based on the elevated concentrations of HPAH in subsurface sediments,
historical levels of contaminant Input were considerably greater than they
are currently. Kaiser Ditch appears to be a continuing source of contamina-
tion, based on:
• Detection of PAH in Kaiser Ditch effluent as recently as
April, 1984
t Elevation of HPAH concentrations in surficial sediments
ironediately off Kaiser Ditch
7.36
-------
HYLEBOS WATERWAY
• Concentrations of PAH in suspended sediments at the head
of the waterway that exceeded those in all other suspended
sediment samples from Commencement Bay.
The proportion of HPAH in the Kaiser Ditch effluent originating from
the wet scrubber sludges, runoff containing particulate matter from atmospheric
emissions, and residual HPAH in ditch sediments cannot be determined.
The relative contribution of these sources will have to be determined in
order to best direct remedial actions.
Kaiser Aluminum and Chemical Corporation and the WDOE are aware of
the potential contamination problems posed by the wet scrubber sludge and
have taken steps to minimize the potential for environmental release.
The following actions have been taken (Fenske, F., personal communication;
Burkhalter, R., personal communication):
t Plant wastewater no longer flows through the sludge-contaminated
ponds prior to discharge to Hylebos Waterway.
• A tide gate has been reinstalled at the mouth of Kaiser
Ditch.
• Surface water runoff from the sludge ponds percolates into
the ground or is diverted through a dike with a filter fabric
prior to discharge to Kaiser Ditch.
• The WDOE is currently reviewing a Kaiser Aluminum and Chemical
Corporation proposal to move sludges now contained 1n three
separate diked enclosures Into a single enclosure, cover
this area with an impermeable cap, and initiate a groundwater
monitoring program for PAH.
Recent and proposed remedial actions should reduce the contribution
of the sludge ponds to the HPAH in Kaiser Ditch effluent. Because the
relative contribution of atmospheric particulate emissions deposited on
plant property and reaching Kaiser Ditch via surface water runoff has not
been established, Kaiser Ditch HPAH loading after stabilization of the
sludge ponds cannot be predicted. The rate at which sediment HPAH concentra-
tions in Hylebos Waterway will reflect a decrease 1n HPAH input cannot
be predicted without additional data on sediment transport and deposition
in the waterway.
The following recommendations may help define other sources of PAH
to Hylebos Waterway:
• Investigate the Naval Reserve facility, drains HY-078 and
HY-076, Sound Refining, PRI Northwest, and Cenex as sources
of LPAH.
• Evaluate HPAH in storm water near the Kaiser facility.
7.37
-------
HYLEBOS WATERWAY
• Continue efforts to stabilize or remove the wet scrubber
sludges. When completed, monitor surface water runoff from
the area to ensure that HPAH do not continue to migrate
to Kaiser Ditch.
• If HPAH input from atmospheric emissions and the sludge
ponds can be curtailed or eliminated, or is found to be
insignificant, remove contaminated sediments within Kaiser
Ditch. These sediments contain up to 300,000 ug/kg PAH
and therefore will represent a continuing source of PAH
to Hylebos Waterway.
7.2.5 Dibenzofuran
7.2.5.1 Spatial Distribution--
The spatial distribution of dibenzofuran in surficial sediments of
Hylebos Waterway is shown in Figure 7.2.17. Dibenzofuran concentrations
in sediments from a broad area between 3,000 and 7,000 ft from the waterway
mouth (Segments 4 and 5) appeared slightly higher than those elsewhere
in the waterway. Sediments from a single station 12,000 ft from the mouth
(HY-22 in Segment 2) were higher than those from surrounding stations.
There was strong similarity between the spatial distribution of dibenzo-
furan in Hylebos Waterway sediments and that of LPAH (Figure 7.2.11).
The correlation between dibenzofuran and LPAH concentrations is discussed
in Section 3.1.5.2. Concentrations of dibenzofuran normalized to organic
carbon were fairly uniform except at Station HY-44 (35 mg/kg T0C). This
station contained 94 percent sand and little organic carbon. The observed
high loading of contaminants when normalized to the small amount of fine-grained
material probably reflects proximity to the source for this coarse-grained
sediment.
Sediment core data indicate that input of dibenzofuran to Hylebos
Waterway was greater historically than at present. Contamination in subsurface
horizons was up to about 20 times greater than 1n the upper horizon.
7.2.5.2 Loading Estimates--
The only discharge to Hylebos Waterway that has been found to contain
dibenzofuran 1s Kaiser Ditch (HK-05Z). Concentrations of approximately
0.7 ug/L dibenzofuran were measured 1n recent samples collected by the
WD0E (unpublished). The following discharges have been analyzed for dibenzo-
furan, although none were detected at 0.1 ug/L: HY-054, HY-066, HY-078,
HY-083, HY-085, and HY-700.
7.2.5.3 Source Identiflcation--
Although dibenzofuran 1s used as an Insecticide (Hawley 1981), this
potential source is not considered significant 1n Hylebos Waterway because
the areas of major dibenzofuran contamination were not associated with
7.38
-------
Segment 6
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Figure 7.2.17
14
16
CONCENTRATIONS OF DIBENZOFURAN IN THE SURFICIAL SEDIMENTS OF THE
HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
Concentrations on a dry weight basis
Concentrations normalized to total organic
carbon content of the sediments
fSj
7.39
-------
HYLEBOS WATERWAY
major sources of runoff (e.g., Hylebos Creek). The strong correlation
between the distributions of dibenzofuran and LPAH (and to a lesser extent
HPAH) discussed previously suggests that sources of LPAH in Hylebos Waterway
probably sources of dibenzofuran (see PAH source identification discussion
in Section 7.2.4.3).
7.2.5.4 Summary and Recommendations--
Dibenzofuran appears to be associated with the distribution of PAH
(especially LPAH) in all areas of Commencement Bay. Contamination of sediments
by dibenzofuran was greater in subsurface sediments than in surficial sedi-
ments. Confirmation of dibenzofuran sources would require substantially
more source loading analyses than are currently available.
Future investigations of potential PAH sources should include analyses
for dibenzofuran, since source identification efforts are hampered by the
absence of data.
7.2.6 Benzyl Alcohol
7.2.6.1 Spatial Distribution--
The distribution of benzyl alcohol in surficial sediments of Hylebos
Waterway is illustrated in Figure 7.2.18. Except for two samples with
relatively high concentrations of the contaminant, benzyl alcohol was dis-
tributed homogeneously from the mouth to the head of the waterway. The
two exceptions were samples from Stations HY-41 (Segment 5, 4,500 ft from
the mouth) and HY-21 (Segment 2, 12,000 ft from the mouth). The former
station was located along the south shore of the waterway, while the latter
was in mid-channel. Neither area had been dredged within the past 10 yr.
The absence of a contamination gradient and the isolation of contamination
to two sites distant from known point sources complicates source identifica-
tion. The single sediment core sample taken in the area of concern (Station
HY-61) had undetectable concentrations (<10 ug/kg) of benzyl alcohol in
all horizons. This indicates either recent input of benzyl alcohol or
degradation of the compound over time.
7.2.6.2 Loading Estimates--
No effort has been made to analyze any discharge to Hylebos Waterway
for benzyl alcohol.
7.2.6.3 Source Identification--
In the absence of effluent and environmental data on benzyl alcohol,
the most feasible way to identify potential sources was to determine types
of industries with which benzyl alcohol may be associated. Benzyl alcohol
has a variety of Industrial uses, many of which are related to the dye
and pigment industry (Hawley 1981):
7.40
-------
Segment 6
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Figure 7.2.18
CONCENTRATIONS OF BENZYL ALCOHOL IN THE SURFICIAL SEDIMENTS OF THE
HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
Concentrations on a dry weight basis
Concentrations normalized to total organic
carbon content of the sediments
iii
7.41
-------
HYLEBOS WATERWAY
• Perfumes and flavors
• Photographic developer for color movie films
• Dyeing nylon filaments, textiles, and sheet plastics
• Solvent for dyestuffs, cellulose esters, casein, waxes,
and other materials
• Heat-sealing polyethylene films
• Intermediate for benzyl esters, benzyl ethers, and benzyl
bromide
• Bacteriostat
• Cosmetics, ointments, and emulsions
• Ballpoint pen inks
• Stencil inks.
In addition, benzyl alcohol is found in jasmine, hyacinth, yling-ylang
oils, and at least two dozen other essential oils (Sax 1984).
None of the industries currently or historically in the areas of elevated
sediment benzyl alcohol concentrations is known to handle dyes, inks, perfumes,
or other products containing benzyl alcohol. The industries nearest the
contaminated areas are Occidental Chemical Corporation, PRI Northwest,
Pennwalt Corporation, and General Metals. Occidental and Pennwalt produce
a variety of inorganic chemicals, PRI Northwest is a petroleum distributor,
and General Metals is a scrap metal dealer. Since none of these industries
or any other industry 1n the areas of contamination handle material containing
benzyl alcohol, there are no known potential sources.
7.2.6.4 Summary and Recornnendations--
A review of the industries in the areas of elevated contamination
was unable to identify potential sources. Because benzyl alcohol is not
a compound typically monitored by regulatory agencies, it may be an unidentified
component of one or more discharges. Benzyl alcohol had been included
among the compounds of concern in this investigation because it has been
found in relatively high concentrations in the livers of some English sole
collected from Hylebos Waterway. This observation and the lack of an apparent
source suggest that benzyl alcohol may be a metabolic product.
Further efforts should be directed towards determining if the elevated
concentrations of benzyl alcohol in fish tissue result from metabolic breakdown
or transformation of another compound.
7.42
-------
HYLEBOS WATERWAY
7.2.7 Chlorinated Hydrocarbons
7.2.7.1 Spatial Distribution-
Three groups of chlorinated hydrocarbons have been designated as contami-
nants of concern in Hylebos Waterway: chlorinated benzenes, chlorinated
butadienes, and chlorinated ethenes. The spatial distributions of these
contaminants in the surficial sediments of Hylebos Waterway are shown in
Figures 7.2.19 - 7.2.24.
The concentrations of two representative chlorinated benzenes (hexachloro-
benzene and 1,4-dichlorobenzene) in Hylebos Waterway sediments are shown
in Figures 7.2.19A and 7.2.20A. Hexachlorobenzene and 1,4-dichlorobenzene
showed an increased concentration (dry weight) at 4,000-4,500 ft from the
mouth of the waterway (Segment 5). The decreases in concentration with
distance from this area suggest the presence of a source in the immediate
vicinity of the observed hot spot. This area of elevated contaminant concen-
trations was still evident after concentrations were normalized to the
organic carbon content of the sediments (Figures 7.2.19B and 7.2.20B).
The enrichment of these compounds in the organic material of these sediments
indicated a nearby contaminant source. A local source of hexachlorobenzene
and 1,4-dichlorobenzene located 3,000 - 4,000 ft from the mouth of the
waterway and independent of major carbon sources is the most likely explanation
for these data. There was no apparent cross-waterway contamination gradient
in this area for either 1,4-dichlorobenzene or hexachlorobenzene, although
there were no data available along the north shore of the waterway (Figure
7.2.21).
For both hexachlorobenzene and 1,4-dichlorobenzene, concentrations
in sediments from a single station 12,000 ft from the waterway mouth were
two to seven times greater than those from neighboring stations. This
station was HY-22, noted earlier to be in an area where recent dredging
has exposed contaminated sediments.
The spatial pattern of chlorinated butadiene contamination (Figures
7.2.22 and 7.2.23) was like that of the chlorinated benzenes, with a pronounced
elevation at 4,000 ft from the waterway mouth on both a dry-weight and
organic carbon-normalized basis. Hexachlorobutadiene concentrations (Figure
7.2.22) also increased at 12,000 ft (Station HY-22). The similarity in
spatial patterns of contamination between the chlorinated benzenes and
butadienes suggests a common source for both contaminant groups.
In December, 1981, Occidental Chemical Corporation sampled sediments
in Hylebos Waterway Segment 5 from the southern shore out to the central
channel (Candler 1982; Moore 1982). Total chlorinated butadiene concentrations
ranged from 1,900 to 25,000 ug/kg along the southern shore of the waterway
at about 3,200 ft from the mouth. More recent data shown in Figure 7.2.22
indicate substantially higher butadiene concentrations further offshore
(up to 47,000 ug/kg).
7.43
-------
Segment 6
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investigations - undetected value
Figure 7.2.19
CONCENTRATIONS OF HEXACHLOROBENZENE IN THE SURFICIAL SEDIMENTS OF THE
HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
(A) Concentrations on a dry weight basis
(B) Concentrations normalized to total organic
carbon content of the sediments
7.44
-------
Segmen
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D
-1—
4
T"
0
D
6
1—
12
Segment 6
"T
_ e 10
(Thousands)
Ft. from mouth of waterway
4 3 2
~
T
B
4 +
—I
14
-1—
16
Benthlc effects
and toxicity
AET
(A)
.O
a
a
H
51
I °
&
Wi
a
8
26 -
24
22
20 H
1B
16
14
12
10 H
8
6
4
2 H
0
O 46.S12 ppb
~
~
r*—
T
O
T"
D q O
T-*T
JZ

Benthic effects
AET > 16000 ppb
(not established)
-------
00D32b^
~100 ^
D120
> Uf2feArP130QUl
A L400^P230*
00
?> *1400 ~"130
^ D56
^ ^ J3180*
500 1000
FEET
-N-
I
~ Exceeds AET (see Table 4.2 for AET values)
O Tttn Ttch ivr>i)f «*ta
A CM tat*
+ WOE, MM *U
X Data fr* otter t|Mcln
Figure 7.2.21
CONCENTRATIONS OF HEXACHLOROBENZENE
In the surficial sediments of HYLEBOS SEGMENT 5
(ug/kg dry weight)
U Indicates undetected at value shown
L At least one of components of the
group was undetected; sum Includes
the detection limit.
7.46
-------
Segment 6
6
X
"5
*
"0
JO
a
- «
,E*o
* D
SS
*1
I
¦D
s
u
c
o
o
22 -i
20 -
1B -
16 -
14 -
12
10
B -
6 -
4 -
2 -3
46.490 ppb^I S 46,980 ppb
j ® 65,540 ppb
a!
°u
T-
2
I
4
-n
-T~
6
T
O
~
~r
—t—
12
Segment
XI
a
a
8^
IS
51
'.I
*
#>
u
c
o
o
2.4 -
2.2 -
2 -
1.8
1.6
1.4 -
1.2 -
1 -
0.8 -
0.6 -
0.4
0.2
C? 15,242,
1 1 r-
8 10
(Thousands)
Ft. from mouth of waterway
4 3 2
A
—r
AO A
AET > 47,000 ppb
(not established)
(A)
14
16
000 ppb
tfio
~ O
T h—
~r
~r
o
up o
A—. f
6 8 10
(Thousands)
Ft. from mouth of waterway
n—
12
M ABi* *1'
Benthlc effects
•nd toxicity
AET
(B)
14
16
OTctn Tech fnvtstlgttlon - qutntfuted vilut
O Other InvMtigitlofis - qutntltited vtlue
A 1*tr» Tech Invfstlgttions • Ins th«n value
~ Tetr« Tech 1nveittg«t1ons - undetected vtlue
Figure 7.2.22
CONCENTRATIONS OF TOTAL CHLORINATED BUTADIENES IN THE SURFICIAL
SEDIMENTS OF THE HYLEBOS WATERWAY WITH DISTANCE
FROM THE MOUTH OF THE WATERWAY
(A) Concentrations on a dry weight basis
(B) Concentrations normalized to total organic
carbon content of the sediments
7.47
-------
Segment 6
5
0.9
X
o>
*5
*
•o
JD
a

,E"o
s ®
S3
M
lw
T>
V
e>
o
c
o
o
0.8 -
0.7 -
0.6
0.5
0.4
0.3 -
0.2 -
0.1 -
ZD.OOP ppb t t~f
a »
_ 3JUU ppb
N»00 ppb
~ D
* O
X
X
o +.
I5J3L..X
_x_
D
~ + Ofr+
*
—m-yr
d° D
Segment
"i ''i 1 r 1 1 1 ^
4 6 8 10 12
(Thousand*)
Ft. from mouth of waterway
4 3 2
© +
+ n + + +
—I—
14
(A)
Benthlc
Effects
AET
Toxicity
AET
16
o
O
x>
a
a
r«;
n O

V
c
o
o
30
25 -
20 -
15
10
5 -
l.KZ.WU ppb
218.60S ppb
T
228 ippb
I
Q
X
—± EIl.
~ ~
do!
X
-0*
4 +

T
T 1 r~
6 8 10
(Thoueonde)
Ft. from mouth of waterway
~r—
12
g *nfl t,+
(B)
Benthlc
Effects
AET
Toxicity
AET
14
16
D Tetr* Tech Investigation - quint1t«ted value
0 Other investigations - quantitated value
~ Tetra Tech investigation - undetected value
1 Other investigations - undetected vilue
Figure 7.2.23
CONCENTRATIONS OF HEXACHLOROBUTADIENE IN THE SURFICIAL SEDIMENTS OF THE
HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
(A) Concentrations on a dry weight basis
(B) Concentrations normalized to total organic
carbon content of the sediments
7.48
-------
Segment 6
*£
*
t
•o
a
a
a.
r>
*>
3
"5
>
T>
V
n
700 -
600 -
500
400
300
c 200 -
u
c
o
o
100 -
J S 350.000 ppb j

< 1
1 1
• 1
I 1

1 1
1 t
1 1
1 1
* 1
1 1
« 1
1 1
1 1
1 1
1 1
1 1

t •
• 1
< 1
1 1
I <
* <
1 1
» 1
1 <
1 1
1 t
* 1
1 1
« 1
1 »
» 1
1 1
* 1

(A)
1 1
« t
< t
1 1
:
t t
• i
i *

l
I
1
I
l
i
1
l
i
~
1
l
1
1
-4-
1
1

Benthlc effects
« •
< t

and toxicity
• nO !
i °Jt

AET
* 'i X .* f \ *, * r-
-T-*-|
¦ * ,
X *
l I l

1
Segment
20 -
> 18 -
16 -
14 -
12 -
10 -
8 -
6 -
4
2 H
o
a
a
t> jj
2%
?§
•>
u
c
o
O
7 9 11
(Thousands)
Ft. from mouth of waterway
13
15
17
32.407,000 ppb
DO
O
T"
2
T
4
1—n 1 r~-i 1 r~
6 8 10 12
(Thousands)
ft. from mouth ef wotsrway
T 1—
14
r~~
16
AET > 22,000
(not established)
(B)
O Tetr* Ttch 1nveit1git1on - quint luted vtluc
OOther tnvesttgitfons - quint luted value
x Other Investigations - undetected vtlue
Figure 7.2.24
CONCENTRATIONS OF TETRACHLOROETHENE IN THE SURFICIAL SEDIMENTS OF THE
HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
(A) Concentrations on a dry weight basis
(B) Concentrations normalized to total organic
carbon content of the sediments
7.49
-------
HYLEBOS WATERWAY
Only 11 surficial sediment samples within Hylebos Waterway were analyzed
for chlorinated ethenes during the Tetra Tech survey, and only tetrachloroethene
was detected (Figure 7.2.24). Tetrachloroethene concentrations were homogeneous
among these stations, most of which were in the central waterway. Previous
investigators have reported very high concentrations of tetrachloroethene
in intertidal and shallow subtidal stations along the southern shore of
the waterway about 3,000 and 12,500 ft from the mouth (Figure 7.2.24).
WD0E (unpublished) reported 350,000 ug/kg in intertidal sediments along
the southern shore of Hylebos Waterway 3,160 ft from the mouth. Candler
(1982) reported up to 69,000 ug/kg in sediments from the same area. Occidental
Chemical Corporation has monitored chlorinated ethenes in the water column
of Hylebos Waterway 2,400 - 4,100 ft from the mouth. Concentrations of
trichloroethene and tetrachloroethene have been as high as 232 and 72 ug/L,
respectively (Conestoga-Rovers and Associates 1984a). The highest values
were typically found along the southern shore of the waterway. There was
some elevation of tetrachloroethene concentrations at 12,000 ft from the
mouth, although not to the same degree as at the 3,000-ft area. As shown
in Figure 7.2.24, Johnson and Prescott (1982) reported up to 740 ug/kg
in intertidal sediments 12,500 to 13,000 ft from the waterway mouth.
The vertical distribution of chlorinated benzenes and butadienes is
shown in Figures 7.2.25 and 7.2.26. The four sediment core samples (only
three are shown) were all taken close to one another in Hylebos Waterway
Segment 5, the area of greatest surficial sediment contamination. The
vertical (temporal) patterns of contamination were not consistent among
all cores, but two generalizations can be made. First, in most cores (including
core HY-63, G01, not shown), the concentrations of chlorinated benzenes
and butadienes increased with depth, indicating that contaminant input
was greater historically than it is at present. Second, the relative proportion
of tri-, tetra-, penta-, and hexachlorobutadienes varied with depth, suggesting
that groundwater rising from deep aquifers is not a major source for these
compounds. If it were, constant relative proportions of the butadienes
would be expected throughout the sediment column. Although not shown,
differences in the relative proportions of the various dichlorinated benzenes
among the horizons also eliminate groundwater from deep aquifers as a source
of these compounds. However, on the basis of the sediment core data alone,
it is not possible to rule out shallow groundwater seeps along the waterway
banks as potential sources.
The only sediment core data available for chlorinated ethenes is a
single sample taken from the deepest horizon (0.66-0.81 m) at Station HY-63,
601. The sediment contained 330,000 ug/kg chlorinated ethenes, indicating
either historical contamination or contamination via groundwater.
In summary, the spatial patterns of contamination of the chlorinated
hydrocarbons suggest that the chlorinated benzenes and butadienes have
a common source. The gradient of contamination along the length of the
waterway suggests that this source is located at about 4,000 ft from the
waterway mouth. The appearance of isolated hot spots along the southern
shore of the waterway suggests that the source of at least the chlorinated
7.50
-------
100
0.2
0.4
100
c

o
0.2 .
0.4 -
0.2
0.4
(A)
Concentration (ug/kg dry weight)
1,000
*«> *
10,000
100
-i—r
! e
'
100,000
' ' * ¦'
I I I I I I)
I Hexachlorobutadlene
benthic effects AET
toxicity AET
i
ii i ii.ii
1,000
I

1,000
¦ ¦ t " I
Pentachlorobutadlene
toxicity AET
(B)
10,000
¦ ¦ ¦ I ¦
* ¦
100,000
'
• ' ¦ • ' •1
(C)
10,000
¦ III
100,000
-ULi
Figure 7.2.25
CONCENTRATIONS OF CHLORINATED BUTADIENES WITH
DEPTH IN THE SEDIMENT COLUMN
(A) STATION HY-63A, B01, (B) STATION HY-63B, B03;
(C) STATION HY-63C, B05
Trlchlorobutadiene (no aet established)
Tetrachlorobutadlene (no aet established)
Pentachlorobutadlene (no benthic effects AET established)
Hexachlorobutadlene
e = estimated concentration
7.51
-------
0.2
0.4
0.2-
c
0)
E
•r—
T5
0»
I/)
E
•r-
CL
01
a
0.4-
0.2
0.4
(A)
Concentration (ug/kg dry weight)
^0 100 1,000
it
II
4J-
l:
i!
1
1. 4 - Dlchloroberizene J:
benthlc effects and *! j
toxlclty AET |'
10
(b|!
100 jj
Oi
I
iii
-rt-
li
I!
A

10,000
¦ ' 1 ¦ ¦ ¦'
Hexachlorobenzene
benthfc effects AET
toxlclty AET
1,000
< I I 11
10,000
i I I I I I t
!!
Si
» i i I
n
(C)j
Hi
II
I:
1,000
10,000
.ulLi
Figure 7.2.26
CONCENTRATIONS OF CHLORINATED BENZENES WITH
DEPTH IN THE SEDIMENT COLUMN
(A) STATION HY-63A, B01; (B) STATION HY-63B, B03;
(C) STATION HV-63C, B05
1,4-dichlorobenzene
hexachlorobenzene
u ¦ undetected at detection limit shown
7.52
-------
HYLEBOS WATERWAY
butadienes may be located along this shoreline. Groundwater from the deeper
aquifiers does not appear to be the major route of contaminant migration.
The chlorinated ethenes had relatively uniform concentrations in the
central portion of the waterway, although there have been several reports
of localized high concentrations in intertidal sediments about 4,000 ft
and, to a lesser extent, about 12,000 ft from the waterway mouth. Based
upon the horizontal and vertical contamination data alone, it is not possible
to establish whether the route of contaminant migration is via industrial
effluent, surface water runoff, or shallow groundwater.
7.2.7.2 Loading Estimates-
Loadings from discharges to Hylebos Waterway with detectable concentrations
of the chlorinated hydrocarbons of concern are summarized in Tables 7.2.4
and 7.2.5. Despite extensive sampling, few discharges were found to contain
measurable concentrations of chlorinated ethenes, chlorinated benzenes,
or chlorinated butadienes. Two groups of discharges require discussion
because of relatively high loading of chlorinated hydrocarbons: those
associated with Occidental Chemical Corporation (HY-707, HY-083, HY-085,
groundwater), with a total chlorinated hydrocarbons loading of 6.6 lb/day,
and those associated with the Pennwalt Corporation (HY-700, HY-701, HY-058,
HY-054, shallow and intermediate aquifers), with a total chlorinated hydrocarbon
loading of 1 lb/day.
Four discharges listed in Tables 7.2.4 and 7.2.5 are associated with
Occidental Chemical Corporation: the main plant effluent (HY-707), pipes
protruding from a bulkhead on the Occidental waterfront (HY-085), and ground-
water discharge beneath the facility (Areas 2 and 3). Loading of chlori-
nated ethenes from groundwater beneath Occidental is the largest identified
in Table 7.2.4. Groundwater beneath Occidental was estimated to contribute
about 6 lb/day chlorinated ethenes. (The method of calculating chlorinated
ethene loading and the locations of Areas 2 and 3 are discussed further
in Section 7.2.7.3). Of this 6 lb/day, 1.5 lb/day was tetrachloroethene;
the remainder was trichloroethene. It is not clear why only tetrachloroethene
was found in the surficial sediments of Hylebos Waterway during the Tetra
Tech survey, when the groundwater beneath Occidental and most other sources
of chlorinated ethenes contributes both tri- and tetrachloroethene. Presumably
it is a function of the greater solubility and lower sediment adsorption
of the trichloroethene.
Loading of chlorinated ethenes from the Occidental Chemical Corporation
main effluent (0.65 lb/day) is also among the largest Identified in Table
7.2.4. This loading is based on a single observation of 5 ug/L chlorinated
ethenes during a W00E Class II survey (Yake 1980). The main effluent is
also identified as a source of chlorinated benzenes and butadienes. Both
hexachlorobenzene (30 ug/L) and hexachlorobutadlene (9 ug/L) have been
detected in the chlorine stripper effluent, which ultimately is discharged
through the main effluent outfall.
7.53
-------
Table 7.2.4
CHLORINATED ETHENES: SUMMARY OF LOADINGS FROM DISCHARGES TO HYLEBOS WATERWAY
Drain f
Drain Naae
Flow (MX)
(Avg. and Range)
(f of Observations)
PrrTod
of Observations
for Contarinant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)
Compounds Detected

IWUSTRI/U. DISCHARGES

HK-052
Kaiser Ditch
1.9
(0.23-2.9)
(n-8)
9/23/80-8/17/81
3.3
&
0.052
trlchloroethene
tetrachloroethene
HT-OS8
PenfwtH Main Outfall
11
(9.4-12)
(n-2)
6/3/80-6/2/81
10
(«-I5)
(n-2)
0.92
trlchloroethene
tetrachloroethene
ht-to;
Occidental (tain Effluent
15.49
(n-1)
9/25/79
5
(n-1)
0.65
trlchloroethene
tetrachloroethene
ntAiRS m
D RUNOFF

m-on
Mornlngslde Ditch
0.66
(0.49-0.78)
(n-3)
9/24/80
1
(n-1)
0.0055
tetrachloroethene
HY-054
East Channel Ditch
0.0055
(0.0014-0.01)
(n-3)
9/23/80-6/2/81
11
(«-17)
(n-2)
0.00050
trlchloroethene
tetrachloroethene
HT-0S6
Six-Inch Concrete
Pipe
0.017
(0.0043-0.029)
(n-2)
6/30/80-8/13/81
240
(52-754)
(n-2)
0.034
trlchloroethene
tetrachloroethene
HY-083
Two Seeps at Occidental
0.00S1
(0.0002-0.01)
(n-2)
4/18/84
L 3.5
(L 3 - L 4)
(n-2)
I 0.00015
trlchloroethene
tetrachloroethene
HT-0B5
Seven Steel Pipes
0.0007
(n-1)
9/23/80-4/18/84
270
(83-450)
(n-2)
0.0016
trlchloroethene
tetrachloroethene
-------

Tab1e7.2.4(cont'd)

GROUNDWATER BANK SEEK

HY-700 Pennwalt East Seep
0.00079
(0.00036-0.0014)
(n-3)
6/3/80-4/1B/84
930
(94-4.830)
(n-4)
0.0061
trlchloroethene
tetrach1oroethene
HY-701 Pennwalt West Seep
0.0012
(0.001-0.0014)
(n-2)
9/23/80-B/13/81
241
(143-395)
(n-3)
0.0024
trlchloroethene
tetrachloroethene
HYLEBOS CREEK

HC-000 Hylebos Creek
MOOt Station 17
16
(4.9-44)
fn-15)
8/17/81
2
(n-1)
0.27
trlchloroethene
GROUMMATER BENEATH PENNUALT

Shallow Aquifer
0.00090
(0.0007B-0.0010)
4/81-9/81
L 1,100
L 0.009*
tet rachloroethene
Intermediate Aquifer
0.0045
(0.0025-0.0066)
4/81-9/81
L 2,045
L 0.11*
tetrachloroethene
GROUNOMTER BENEATH OCCIDENTAL

Area 2
0.0014
12/79-9/84
313,000
(202,000-529.000)
(n-14)
(2.4-6.2)
trlchloroethene
tetrachloroethene
Area 3
0.0016
12/79-9/84
165,000
(8,000-299,000)
(n-14)
2.2*
(0.11-3.9)
trlchloroethene
tetrachloroethene
NOTES: L Indicates less than
* Loading estimated froa data 1n AUAftE (1961), sn text
b Loading estimated by procedures 1n Walker Hells (1980a), see tent
Ttie following discharges have been sanpled and found not to contain chlorinated ethenes (numbers In parentheses Indicate number of analyses
and detection Halts): HC-130 (1. 1 ug/1). HT-016 (1. 1 ug/1), HY-017 (1, unspecified), HY-018 (1, 4 ug/1), HY-0Z1 (1, 10 ug/1), HY-023 (1.
10 1/9/I), HY-040 (1, 1 U9/1), HY-061 (1, 1 ug/l), HY-066 (3, 1-10 ug/1), HT-071 (1, unspecified), HY-073 (I. 1 ug/1), HY-076 (I. 10 ug/1),
HY-078 (2, 1 ug/1), HY-704 (2, unspecified). HY-709 (2. 1 ug/1).
-------
Table 7,2.5
CHLORINATED BENZENES AND BUTADIENES: SUMMARY OF LOADINGS FROM DISCHARGES TO HYLEBOS WATERWAY
CHLORIMTEO tOgEMCS
Oraln 1 Drain hit
Flow (TO)
(A*g. and Range)
(f of Observations)
Period
of Observations
far Cwita«1n»nt
Concentration
Concen-
tration (ug/1)
(Avg. and Range)
<» of Observations)
loading {\bsfity)
(Avj. end Range)
Compounds Detected
INDUSniAL DISCHARGES

Hr-707 Occident*1 Ha la Effluent
IS. 49
£i)
mvn
0.3
(
0.039
hexach F orobenzene
Huaas ckck

HC-000 iferlebM Creek
MBOE Station 17
16
(4.9-44J
{»•«)
11/7/83
L 3
£i>
L 0.40
l,3-d1cMoroben*erte
OWIKS MO RUNOFT

HM-OZ8 Ptornlngslde Ditefc
0.(C
10.W-O.7B)
(n-3)
8/17/81-11/7/83
L 38
R - t 85)
ln-2)
I 0.?l
(0.1! - t 0.47)
1.2-dlcfelorobenzene
1.3-dlcklorobenrene
1 .(-dldilorobenzene
1,2,4-t rtcM orobenzene
KY-085 Seven Steel Mpes at
Occidental
O.OOC7
(¦•1)
9/23/80
L 11
tmli
L 0.00006
1,Z-dIchlorobentene
1.3-dlchlorobentene
ttOUMMATCft tNK SCEPS

W-70C fennwalt Em Seep
0.000J9
(0.00036-0.0014)
(n-3)
9/23/80
9
(n»l)
0.000059
1,2,4-trIchlorobeniene
MOTE: Ttw fotlottittq discharges have been sampled end found net to contain chlorinated benzenes (nunbert In parentheses Indicate n«ber of analyses and
detection ltalts): HC-130 (1, 1 m/1), HT-C52 (U, 1-iQ flj/l), Wf-OlS (1. I uS/1), HT-017 (1, unspecified), Hr-OIB (1. 0.5-8 119/1), HY-tKl (1. 10
«9/l). HT-C23 (1, 10 ug/1), HT-040 (I, 1 ug/t), NT-0S4 (3. 1-10 119/I). HT-056 (I. unspecified), HT-058 {1, unspecified). HT-061 (1. 1 u9/1).
HT-062 (1, J ub/1), mr-066 (3, 1-10 Bt/1), trr-070 (1. 1 ug/1), H1-0T1 (1, I«we«f1edl, HT-073 (u 1 U9/1K KT-078 (I, 10 09/!), «*-«78 (2, 1
ug/l), HT-083 (2, 1 vg/lj, KT-700 (3. 1 uj/1). HT-701 (!, 1 ug/l), KY-704 (2, unspecified), HT-709 (1, unspecified).
-------
Table7.2.5(cont'd)
CHLORINATED BUTADIENES
INMISTRIM. DISCHARGES

HY-707 Occidental Main Effluent
15.49
(n*l)
9/25/79
0.2
(*•1)
0.026
hexachlorobutadlene
DRAINS MB MMOFF

HY-085 Seven Steel Pipes at
Occidental
0.0007
(n-1)
9/23/80-4/18/84
3.5
(2-5)
(n-2)
0.000020
(0.000012-0.000029)
tr1ch1orobutad1ene
tetrachlorobutadlene
hexachlorobutadlene
SMXMMITER BMK SEEPS

HY-700 Pewwalt East Seep
0.00079
(0.00036-0.0014)
(n-3)
9/23/80-4/18/84
&
0.000040
(0.000033-0.000046)
hexachlorobutadlene
HT-701 Penmalt West Seep
0.0012
(0.001-0.0014)
(n-2)
9/23/80-6/2/81
I 5
a i-9)
(n-2)
L 0.00005
(I 0.00001-0.00009)
hexachlorobutadlene
NOTES: The foilowl 114 discharges have been iaapled am) found not to contain chlorinated butadienes (nutters In parentheses Indicate nunber of analyses
and detection Halts): HC-000 (5, 1-20 ug/1), HC-130 (1, 1 ug/1), HK-052 (II, U10 ug/1). HN-028 (6, 1-20 ug/1). HY-016 (1. 1 ug/1). HY-01B (1,
8 ug/1). HY-021 (1. 10 ug/1), Mt-023 (1. 10 ug/1), HY-040 (1. 1 ug/1), HY-054 (4, 1-10 ug/1). HY-056 (2, 1 ug/1), HY1-058 (1, unspecified).
HT-062 (1. 1 ug/1), HY-062 (1. 1 ug/1), HY-066 (3. 1-10 ug/1), HT-070 (1, 1 ug/1), HT-071 (1. unspecified), HT-076 (1. 10 ug/1). HY-078 (Z. 1
«g/l). HT-083 (2, 1 ug/1). HY-709 (2, 1 ug/1)
L Indicates less than
-------
HYLEBOS WATERWAY
The Pennwalt main outfall (HY-058) is a known source of chlorinated
ethenes (0.92 lb/day), although concentrations of chlorinated benzenes
and butadienes have been below detection limits.
Four discharges shown as known sources are associated with groundwater
beneath the Pennwalt Corporation property: the East Seep (HY-700), the
West Seep (HY-701), and the shallow and intermediate aquifers. The Pennwalt
seeps are sources of chlorinated benzenes, chlorinated ethenes, and chlorinated
butadienes (Osborne 1980a, 1980b). Chlorinated ethene loadings from the
shallow and intermediate aquifers have been estimated from chloroform loading
as discussed in Section 7.2.6.3. The values shown should be considered
as approximate upper limits; actual loading could be significantly lower.
Hylebos Creek is indicated as a source of chlorinated ethenes in Table
7.2.4 because of a single observation of 2 ug/L trichloroethene (WDOE unpub-
lished). It is listed as a source of chlorinated benzenes because of a
single observation of <3 ug/L 1,3-dichlorobenzene (WDOE unpublished).
The fact that the contaminated sediments were distant from the point of
discharge of Hylebos Creek indicates that the creek is not responsible
for the observed contamination in the areas of concern. Chlorinated benzene
loading from the Morningside Ditch (HM-028) is based on a concentration
of <38 ug/L. Chlorinated benzene concentration has, on at least one occasion,
exceeded this value (<85 ug/L; WDOE unpublished). It is unknown if this
represented a single occurrence or an unidentified sporadic discharge.
Nevertheless, Morningside Ditch discharges to Hylebos Waterway on the north
shore and the area with elevated chlorinated benzenes is along the south
shore. Therefore, Morningside Ditch is probably not the source of the
observed contamination.
7.2.7.3 Source Identification--
The distribution of both chlorinated benzenes and butadienes in the
surficial sediments of Hylebos Waterway suggests the presence of a source
in Segment 5, about 4,000 ft from the mouth of the waterway. Given its
proximity to the contaminated area and its known discharges of tne compounds,
this source is the Occidental Chemical Corporation.
The chlorinated ethenes have not been found at elevated concentrations
within surficial sediments of the central waterway, although localized
hot spots have been reported In intertidal and shallow subtidal areas along
the southern shoreline. These hot spots have been found in Hylebos Waterway
Segment 5, about 3,200 ft from the waterway mouth, and Segment 2, about
12,500 ft from the mouth. Occidental Chemical Corporation and Pennwalt
Corporation are the major sources for these contaminants 1n Segments 5
and 2, respectively, based on their proximity to the hot spots and known
discharges of the chlorinated ethenes. Occidental Chemical Corporation
and Pennwalt Corporation are discussed individually below.
Occidental Chemical Corporation--Occidental Chemical Corporation occupies
the south shore of Hylebos Waterway between 3,100 and 4,400 ft from the
mouth of the waterway. Chlorinated hydrocarbons, particularly the chlorinated
7.58
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HYLEBOS WATERWAY
ethenes, have been produced at the Occidental Chemical Corporation facility
either as a product or a by-product of past and present industrial practices.
Two independent manufacturing practices at the plant can be identified
as potential sources of chlorinated ethenes, benzenes, and butadienes:
(1) the production of chlorine and caustic soda by electrolysis of sodium
chloride brine and (2) operation of the solvents production facility.
The chlorinated ethenes are considered by-products from the use of
graphite anodes in the production of chlorine (AWARE 1981). Chlorinated
benzenes are a by-product in the manufacture of chlorine gas by electrolysis
of brine (Konasewich et al. 1982). Hexachlorobutadiene is used by chlorine
producers, to recover chlorine from "snift" gas (U.S. EPA 1980a). Occidental
currently uses a sodium hypochlorite countercurrent system for this purpose
(Monahan, F., personal communication); past practices have not been determined.
The manufacture of chlorine and sodium hydroxide by electrolysis began
at the Occidental Chemical Corporation site in February, 1929 with the
opening of the Tacoma plant, and continues to the present time. Historically,
the anode used in this electrolytic process was made of graphite impregnated
with linseed oil to prevent deterioration. (The firm has replaced some
of the graphite anodes with titanium anodes.) Reaction of free chlorine
with the linseed oil in the graphite results in the production of a number
of chlorinated organic by-products. These chlorinated organic compounds
leave the electrolytic cell along with the chlorine gas and are processed
by direct and/or indirect cooling (Figure 7.2.27). At this point, the
waste stream is split into two components. One portion continues through
drying, compression, and purification processes. The second component
is directed to a chlorine stripper for recovery of remaining chlorine gas.
From 1929 to 1969 or 1970, effluents from both the chlorine purification
unit and the chlorine stripper were discharged directly to Hylebos Waterway
through the main effluent (Boys and Sceva 1979). Since 1969 or 1970, the
chlorinated organics from the chlorine purification unit have been taken
out-of-state for incineration and have not been released to Hylebos Waterway
(Boys and Sceva 1979). The effluent from the chlorine stripper continues
to be discharged to Hylebos Waterway along with the total plant effluent.
It is difficult to estimate the concentration or loading of chlorinated
organics in the Occidental Chemical Corporation effluent over the 40 yr
during which effluent from both the chlorine purifying unit and chlorine
stripper was discharged to Hylebos Waterway. In 1979, 50-75 gal/day of
chlorinated organic wastes were generated by the chlorine purifying unit
at Occidental (Boys and Sceva 1979). However, historical volumes may have
been much lower because production capacity was probably smaller. It may
be possible, by analysis of the wastes from the chlorine purifying unit
and review of plant records, to determine the historical composition of
this waste stream and loading estimates of the Individual components.
Recent information is available regarding effluent from the chlorine
stripper. Yake (1980) reported that the chlorine stripper effluent contained
a variety of chlorinated organics Including tetrachloroethene (30 ug/L),
hexachlorobenzene (30 ug/L), and hexachlorobutadiene (9 ug/L). These concentra-
7.59
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Spant Sulfuric Add
Sulfuric
Acid
Electrolytic
Call*
O*
O
Direct and lor
Indirect
Cooling
Drying
Cflwp rn don
Chlorinated
CMorlna
Stripper
CMorlna Cat
Purification
Chlorinated
Organic
Storage
Liquefaction
Sales
[
rom 14H to MiTO:
To Hylebos;
Post-1»7D: To
Incineration
StMM
pH Control
Systan
Plant
Effluant
Caustic
Soda
Process
Figure 7.2.27
FLOW SCHEMATIC OF CHLORINE PRODUCTION AND CHLORINATED ORGANIC WASTE HANDLING
AT OCCIDENTAL CHEMICAL CORPORATION (Modified from OCC, 1984a)
-------
HYLEBOS WATERWAY
tions were reduced by dilution in the total plant effluent to 4, 0.3, and
0.2 ug/L, respectively.
A second potential source of chlorinated organic compounds at Occidental
Chemical Corporation was the solvents plant. This facility produced trichloro-
ethene and tetrachloroethene between January, 1947 and May, 1973. The
plant produced about 500 tons/yr of "Generator and Stripper Lime" waste
that consisted of calcium chloride, excess lime, inert inorganic solids,
and chlorinated organic compounds (Boys and Sceva 1979). Occidental Chemical
Corporation has estimated that the solids in this waste contained 3,000
- 4,000 ppm chlorinated organic compounds (Feller 1981). Contaminants
associated with this waste include dichloromethane, chloroform, carbon
tetrachloride, trichloroethene, and tetrachl oroethene (Walker Wells 1980a).
Hexachlorobutadiene, a by-product of the manufacture of chlorinated ethenes
(U.S. EPA 1975), could also have been among the chlorinated organic compounds
in the wastes.
The Occidental Chemical Corporation solvent plant began operation
in 1947. Its waste disposal history (Boys and Sceva 1979) is as follows:
1947-approximately 1950 All wastes discharged to Hylebos Waterway.
1950-approximately 1952 Wastes discharged to pond located along northwest
plant boundary, now occupied by salt pad. Liquid
decanted to Hylebos Waterway.
1952-1972
1972-April, 1972
Wastes discharged to lime barge moored in Hylebos
Waterway. Liquids decanted overboard to Hylebos
Waterway. Solids barged to Commencement Bay deep-
water disposal site.
Wastes discharged to one of two pits In southwest
corner of plant property. Liquids decanted to
Hylebos Waterway. Solids trucked Tacoma Municipal
Landfill.
May, 1972-June, 1972
Wastes discharged to above pits. Liquids decanted
to Hylebos Waterway. Solids trucked to "Petarcik"
site, 2.5 km west of Fife.
June, 1972-May, 1973
May, 1973
Wastes discharged to above pits. Liquids decanted
to Hylebos Waterway. Solids trucked to "General
Metals" site on north shore of upper Hylebos Waterway
and "Don Ollne" property, 0.8 km southeast of
Occidental plant.
Plant operation terminated.
To assess the extent of chlorinated organic contamination on plant
property as a result of solvents plant operation, Occidental Chemical Corpor-
ation contracted Walker Wells, Inc. and Hart-Crowser and Associates to
7.61
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HYLEBOS WATERWAY
conduct groundwater and soil chemistry studies on the plant property and
on adjacent Port of Tacoma land to the northwest. Results of this work
have been released in a series of documents (e.g., Hart-Crowser 1980a;
Walker Wells 1980a,b). Groundwater quality measurements made at 12 sites
throughout the area (Figure 7.2.28) organic compounds in the vicinity of
wells 1, 4, 7, 10, 11, and 12, with total chlorinated organics concentration
reaching about 700 mg/L. The chlorinated organic compounds with the greatest
concentrations in groundwater were methylene chloride, chloroform, chlorinated
ethanes, and chlorinated ethenes. Hexachlorobutadiene was detected in
a single well (#4) at up to 960 ug/L. Chlorinated benzenes were undetected
at 10 ug/L (Walker Wells 1980b, Appendix B). Contamination was observed
in the shallowest wells (24 ft) down to a depth of at least 115 ft (Site
4). In general, concentrations of chlorinated organics decreased with
depth (Walker Wells 1980b). Walker Wells (1980a) estimated that 19,000
- 35,000 lb of chlorinated organic compounds were contained in the saturated
zone beneath the Occidental facility. Using the percentage composition
provided by Walker Wells (1980a, Appendices D and E) for each compound
within the chlorinated organic group, trichloroethene constitutes an estimated
9,000 - 15,000 lb of this total, while tetrachloroethene constitutes an
estimated 900 - 1,500 lb.
To refine the location of chlorinate organic hot spots in the unsaturated
zone, Hart-Crowser and Associates collected soil samples from 69 test pits
and auger holes (Hart-Crowser and Associates 1980a,b; Walker Wells 1980a).
Samples were concentrated in three areas where chlorinated organics would
most likely be found on the basis of historical industrial practices.
The areas sampled are shown in Figure 7.2.28 and include Area 1, beneath
the construction storage/parking lot at the site of an old settlement pond;
Area 2, in the vicinity of the old solvents plant, solvents plant sludge
pits, and abandoned trichloroethene tanks; and Area 3, surrounding an old
trichloroethene tank. Areas 2 and 3 were the most contaminated, with one
Area 2 sample containing a chlorinated organics concentration of 20,000
mg/kg. Concentrations of chlorinated organic compounds generally increased
with depth down to 7 - 8 ft, the lower limit of sampling. Hart-Crowser
and Associates (1980b) estimated that 10,724 lb of chlorinated organic
compounds were contained in the unsaturated zone within these three areas,
most of which (9,363 lb) was 1n Area 2.
As a result of these Investigations of the unsaturated zone, the WD0E
ordered Occidental Chemical Corporation to remove all soils 1n Areas 2
and 3 containing over 150 mg/kg chlorinated organic compounds and to cover
all areas in excess of 15 mg/kg with an impermeable material (Docket No. DE
81-153). These actions have been completed, and 1t has been estimated
that the excavation resulted 1n removal of 9,368 lb (or 87.4 percent) of
the total chlorinated organics previously quantified (Walker Wells 1980b).
No action was taken on the contaminated groundwater because of the ineffective-
ness of existing removal/treatment technology, and because dilution calculations
indicated only a small impact on receiving water column quality (Walker
Wells 1980b; unreferenced status report in WD0E Occidental Chemical Corporation
files).
7.62
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HYLEBOS WATERWAY
Since removal of the contaminated solids in Areas 2 and 3 in 1981,
Occidental Chemical Corporation has continued to monitor groundwater quality
in three wells on a quarterly basis. (A fourth well was monitored through
February, 1982, but monitoring was discontinued since contaminant concentrations
were typically all below the detection limit of 1 ug/L). Trends in groundwater
quality in Well 4 beneath Area 2 (see Figure 7.2.28), based on quarterly
analytical reports submitted to WDOE by Occidental, are shown in Figure
7.2.29. Trichloroethene concentrations have not shown a consistent trend
since removal of the overlying contaminated soils in the spring of 1981.
Tetrachloroethene and total chlorinated hydrocarbons (chlorinated ethenes,
chloroform, and methylene chloride) concentrations have increased in ground-
water. Average chlorinated hydrocarbon concentrations in Well 1 beneath
Area 3 have also shown an increasing trend (64 ug/L before soil removal;
533 mg/L after soil removal). Contaminant concentrations in Well 7 near
Area 1 have decreased (223 ug/L before soil removal; 71 ug/L after soil
removal). In general, the soil removal ordered by WDOE has not yet resulted
in a noticeable improvement in groundwater quality. However, a rapid
improvement should not be expected given the low permeability of the water-
bearing materials (Walker Wells 1981).
The data discussed above were used to calculate the chlorinated ethene
loading presented in Table 7.2.4. Averages of all tri- and tetrachloro-
ethene concentration measurements from December, 1979 to September, 1984
were calculated for Well 1 (representative of Area 3) and Well 4 (representa-
tive of Area 2). Groundwater discharge rates taken from Walker Wells (1980a)
were then used to calculate loadings. The procedure used to calculate
loadings followed that of Walker Wells (1980a), with the exception that
their contaminant concentrations were based only on the July, 1980 data,
a date when contaminant concentrations were relatively low.
Hylebos Segment 2 - Pennwalt Corporation--An area of elevated chlorinated
ethene concentrations was located In Hylebos Segment 2 at 12,000 ft from
the mouth of the waterway, corresponding to the portion of waterway bordered
to the south by Pennwalt Corporation. Pennwalt has been located at its
present site along Hylebos Waterway since the 1920s. The plant produced
chlorine, sodium hydroxide, chlorate salts, and herbicides, and, except
for herbicides, continues to produce these materials.
The chlorinated organic compounds created at Pennwalt as by-products
of chlorine production are separated from the chlorine gas during passage
through cooling towers. Pennwalt historically discharged the condensate,
containing chlorinated organic compounds and residual chlorine, to on-site
evaporation lagoons 1n an area known as Taylor Lake (see Figure 7.2.30).
Graphite wastes from the anodes, which were likely to have been contaminated
with chlorinated organic compounds, were historically disposed of 1n the
Taylor Lake area (AWARE 1981).
As a consequence of these past waste disposal practices, groundwater
beneath the Pennwalt facility has become contaminated by a variety of chlori-
nated organic compounds. From April to September, 1981, AWARE, Inc. conducted
a groundwater quality survey on the Pennwalt property. Initial sampling
7.63
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Scale (in meters)
0 30 60 90 120
HYLEBOS WATERWAY
bock #1
=3
gArea 3g

/ ¦y
Alexander Avenue
House
T ransformer
Yard
e
o
Figure 7.2.28
LOCATION OF GROUNDWATER MONITORING WELLS
AT OCCIDENTAL CHEMICAL CORPORATION
-------
1400
1200
1000
800
Total
C 600
400
200
Trichloroethene
Tetrachloroethene
••
• ••
• §• • •
§
•—t CSJ
eo co
CSJ (Si
c\i
co
n
oo
m
co
vp
o
Sampling Date
NOTE: 0ATA SHOWN ARE FROM HELL NO.4. LOCATED IN AREA 2. SAMPLES HERE COLLECTED
AT SCREENED DEPTHS OF 45 FT. SAMPLE COLLECTED 12/79 HAS ANALYZED BY CAN
TEST. ALL OTHER SAMPLES HERE ANALYZED BY OCCIDENTAL CHEMICAL CORPORATION.
Figure 7.2.29.
CONCENTRATION OF CHLORINATED ORGANIC COMPOUNDS IN GROUNDWATER
BENEATH OCCIDENTAL CHEMICAL CORPORATION.
7.65
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HYLEBOS WATERWAY
Plant Efflu«nt
_e
#ND
LA-PACIFIC
20 # #380 #430
6f
Scale (in meters)
Tr
TAYLOR LAKE
AREA
SALT
STORAGE
U.S. GYPSUM
WALLOW
AREA
PRODUCTION AREA
ND
#ND
Taylor Way
ND
AC CHEM
REICHHOLO CHEMICALS
L.B. FOSTER WAREHOUSE
Concentration of tetrachloroethylene tug/I)
ND Not Detected
Tr Trace
Figure 7.2.30
CONCENTRATIONS OF TETRACHLOROETHENE IN GROUNDWATER MONITORING WELLS
ON THE PROPERTY OF PENNWALT CORPORATION. (Data from AWARE, 1981)
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HYLEBOS WATERWAY
was restricted to an intermediate aquifer (15-20 ft deep) and a deep aquifer
(45 ft deep). Chemical analyses of groundwater in these aquifers indicated
elevated concentrations of arsenic, chromium, and volatile organic compounds
(chloroform, carbon tetrachloride, chlorinated ethanes, and chlorinated
ethenes). Among the compounds identified to be of concern in the present
investigations (chlorinated ethenes, chlorinated benzenes, and chlorinated
butadienes), only tetrachloroethene was consistently found in elevated
concentrations. The concentrations of tetrachloroethene in various monitoring
wells on the Pennwalt property are shown in Figure 7.2.30, indicating that
the contamination was generally restricted to the area between Taylor Lake
and Hylebos Waterway. Subsequent sampling of a shallow aquifer (10 ft
deep) and additional sampling of the intermediate and deep aquifers by
AWARE indicated that contamination of groundwater by tetrachloroethene
was generally restricted to the shallow and intermediate aquifers. Trichloro-
ethene was only detected in trace amounts, while chlorinated benzenes were
undetected. Hexachlorobutadiene was detected in a single well north of
Taylor Lake at 16 ug/L. Its occurrence was attributed to historical disposal
of solvents in the Taylor Lake area (AWARE 1981).
Chlorinated ethenes were not compounds of major concern in the AWARE
surveys and the data are inadequate to directly compute tetrachloroethene
loadings. Samples were frequently not analyzed for tetrachloroethene in
the most contaminated areas, samples were lost, or only composite samples
were taken. However, tetrachloroethene loading may be estimated indirectly
using data for chloroform, a compound of major concern in the AWARE studies
and one for which a great deal of groundwater quality data are available.
During the AWARE studies, 64 samples were analyzed for both chloroform
and tetrachloroethene. Of these, 24 had concentrations of both compounds
below detection limits. Concentrations of both compounds in the remaining
40 samples are shown in Table 7.2.6 and Figure 7.2.31. Chloroform and
tetrachloroethene concentrations were frequently elevated in samples from
the same stations. Tetrachloroethene concentrations were typically less
than half those of chloroform. A direct linear relationship between the
two compounds could not be established, largely because of the single outlier
(chloroform = 5,840 ug/L, tetrachloroethene = 180 ug/L), shown in Figure
7.2.31. Chloroform and tetrachloroethene were by-products of the same
chlorine production process at Pennwalt, disposed in the same manner (on-site
lagoons in the Taylor Lake area), and have similar environmental fate processes
(primarily volatilization; Callahan et al. 1979). Therefore it is possible
to use the concentration of one compound to predict, or at least place
constraints on, that of the other.
AWARE (1981) determined an average chloroform concentration in the
groundwater contaminant plume north of Taylor Lake and, along with estimates
of discharge rate, estimated groundwater chloroform loading in the shallow
(0.014-0.018 lb/day) and intermediate (0.085-0.22 lb/day) aquifers. If
the tetrachloroethene concentration is considered to be half or less that
of chloroform, the tetrachloroethene loading via groundwater can be estimated
at less than 0.009 lb/day from the shallow aquifer and less than 0.11 lb/day
from the intermediate aquifer. Actual loadings could be considerably less.
While the absence of data preclude calculating a more precise loading for
7.67
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Table 7.2.6
AWARE (1981) GROUNDWATER SAMPLES CONTAINING CHLOROFORM AND/OR
TETRACHLOROETHENE CONCENTRATIONS ABOVE DETECTION LIMITS
Chloroform Tetrachloroethene
Sampling Monitoring Concentration Concentration
Round Well (yq/1) (yq/1)
First PW-1C 1,300 430
PW-2C 1,800 380
PW-3C 170 20
PW-4C 160 10
PW-5C <10 <10
PW-6C <10 <10
PW-7C <10 <10
PW-8C <10 <1
PW-9C <10 <1
PW-10C <10 <1
PW-11C <10 <1
Second PW-2S-LT-2 2,700 860
PW-2S-HT-2 5,840 180
PW-3S-LT-2 390 <0.01
PW-3S-HT-2 160 0.4
PW-4S-LT-2 9 <0.01
PW-4S-HT-2 43 <0.01
PW-5S-LT-2 3 <0.01
PW-6S-LT-2 4 <0.01
PW-6S-HT-2 <2 0.01
PW-7S-HT-2 2 0.01
PW-8S-HT-2 <2 2.5
PW-9S-LT-2 <2 0.01
PW-9S-HT-2 <2 1
PW-10S-HT-2 <2 0.4
PW-11S-HT-2 <2 0.4
PW-12S-HT-2 590 340
PW-2D-LT-2 2 0.9
PW-3D-LT-2 2 0.3
PW-4D-LT-2 310 0.1
PW-4D-HT-2 68 <0.01
PW-5D-HT-2 3 0.01
PW-6D-LT-2 <2 0.01
PW-10D-LT-2 2 0.01
PW-12D-HT-2 8 18
Third PW-4SS-HT 996 <0.01
PW-4SS-LT 408 <0.01
PW-6SS-HT 840 20
PW-6SS-LT 835 10
PW-10SS-LT 16 0.6
7.68
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/
/
/
/
/
/
/
/
/
/
/
^°V
&
*s
*>v
<06V
\oy
.v
*y * ^
/ y, V°>
/ y^>
/ ^
/ ^ .
/ ^
/ TCE = 180 ug/l
/^ *
Chloroform = 5840 ug/l
im-M-—• • • ^ 1 t
1000 2000 3000
Chloroform Concentration (yg/l)
Figure 7.2.31
RELATIONSHIP BETWEEN CHLOROFORM AND TETRACHL0R0ETHENE
CONCENTRATIONS IN GROUNDWATER BENEATH THE PENNWALT PROPERTY
(Data from AWARE, 1981)
7.69
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HYLEBOS WATERWAY
the compound, the above exercise places reasonable upper limits on actual
loadings.
Contamination of groundwater at Pennwalt by chlorinated organic compounds
is a consequence of historical rather than current disposal practices.
Since 1981, the chlorine condensate, previously disposed in the on-site
lagoons, been passed through a chlorine stripper and discharged to Hylebos
Waterway through the main outfall (Yake 1981). A single analysis of the
main outfall effluent after this rerouting of the chlorine condensate did
not detect measurable levels of chlorinated ethenes (Yake 1982a; detection
limits unspecified). The graphite anodes impregnated with linseed oil
that had historically been used were replaced with titanium anodes in 1975
(High, 0., personal communication), thereby reducing production of chlorinated
organic by-products.
7.2.7.4 Summary and Recommendations--
Based on review of the existing data, Occidental Chemical Corporation
appears to be the major source of the chlorinated benzenes and butadienes
found in Hylebos Waterway sediments. A single sediment station with elevated
chlorinated benzene and butadiene concentrations off Pennwalt Corporation
was located where buried sediments had probably been recently exposed by
dredging. It is unknown whether contamination of these previously buried
sediments can be attributed to Pennwalt, Occidental, or some other source.
Discharge of chlorinated benzenes has been documented from Morningside
Ditch and Hylebos Creek, although the spatial gradient of contamination
strongly suggests that Occidental is the major source.
Both Pennwalt Corporation and Occidental Chemical Corporation are
sources of tri- and/or tetrachloroethene. Based on both the extent of
sediment contamination and calculated loadings, Occidental appears to be
the larger of the two sources. These compounds have been released from
the facilities through both groundwater and the main plant outfalls. Although
localized contamination of intertidal sediments by chlorinated ethenes
has been found at both Pennwalt and Occidental, the distribution of chlorinated
ethenes in sediments of the central waterway appears relatively homogeneous.
Extensive sampling throughout the waterway has not been conducted for these
volatile compounds. Findings pertinent to Occidental and Pennwalt are
summarized below.
Occidental Chemical Corporation—Occidental Chemical Corporation is
the major source of the chlorinated organlcs compounds of concern to Hylebos
Waterway for the following reasons:
• An Increase 1n concentrations of chlorinated organic compounds
in waterway sediments adjacent to the facility as compared
to concentrations throughout the remainder of the waterway
• The fact that Occidental is the only Industry, both presently
and historically, in the area of greatest contamination
7.70
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HYLEBOS WATERWAY
• A greater estimated loading of chlorinated benzenes, butadienes,
and ethenes to Hylebos Waterway from this facility than
from any other along the length of the waterway
• The documented discharge of a variety of industrial process
effluents directly into the Hylebos Waterway, all of which
could contain one or more of the contaminants of concern
• Detection of all chlorinated organic compounds of concern
in the main plant discharge
t Contamination of soil on the plant property by chlorinated
organic compounds as a result of past spills and waste disposal
practices
• Contamination of groundwater beneath the plant property
by chlorinated ethenes
• Detection of chlorinated ethenes in water samples collected
from Hylebos Waterway near the facility.
Based on the production history of Occidental Chemical Corporation,
discharge of chlorinated organic compounds to Hylebos Waterway was probably
greater in the past than 1t is at present. Until the early 1970s, chlori-
nated organic compounds were released to Hylebos Waterway via discharges
from the chlorine purifying unit, the chlorine stripper, the solvents plant,
and groundwater. The groundwater and the chlorine stripper effluent (via
the main outfall) still introduce chlorinated organic compounds to the
waterway. A decrease in chlorinated organic discharge over time is reflected
in most of the sediment core samples taken off Occidental.
At the present time, chlorinated organic compounds are reaching Hylebos
Waterway sediments from both the main Occidental outfall (chlorinated benzenes,
butadienes, and ethenes) and through groundwater (chlorinated ethenes).
Documentation of the chlorinated benzenes and butadienes 1n the main plant
outfall is based on the 1979 Class II survey. Additional analysis 1s recom-
mended .
The WDOE has started to address the problem of groundwater contamination
by ordering removal of contaminated soil and covering of the contaminated
areas with an impermeable material (asphalt). Although contaminants already
in the saturated zone will continue to reach the waterway, these actions
should result in a continued improvement 1n groundwater quality with time.
However, as of late 1984 (3 yr after remedial action), no improvement in
groundwater quality was evident and continued monitoring appears warranted.
Pennwalt Corporation--Pennwalt appears to be responsible for the chlor-
inated ethene contamination of 1ntert1dal sediments 1n upper Hylebos Waterway,
for the following reasons:
7.71
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HYLEBOS WATERWAY
• An increase in the sediment concentrations of chlorinated
ethenes in Hylebos Waterway adjacent to the facility
• Detection of chlorinated ethenes in water samples collected
from Hylebos Waterway adjacent to the facility (Osborne
1980)
• The production of the chlorinated compounds of concern during
chlorine production at the facility
• Detection of chlorinated ethenes in groundwater beneath
the facility and/or in groundwater seeps along the facility's
waterfront
• Detection of chlorinated ethenes in the main plant effluent.
Chlorinated ethenes have migrated from the facility to the waterway
via three principal routes: discharge via the main outfall effluent, stormwater
runoff from on-site waste ponds, and groundwater discharge from the shallow
and intermediate aquifers. Cessation of discharges to the on-site waste
ponds in 1981 should have reduced the release of contaminants by surface
water runoff.
Contamination via groundwater continues as a consequence of historical
disposal of wastes 1n the Taylor Lake area. Groundwater is currently a
potential source of chlorinated ethenes to Hylebos Waterway, although not
to the extent as groundwater is at Occidental. Based on detection of hexachloro-
butadiene in groundwater and seeps along the waterfront, it appears that
this compound is also entering the waterway via groundwater, although the
loading estimates do not Indicate that this is a major source. If remedial
action is taken, efforts should first be directed towards removing the
sources of the contamination at Pennwalt. These efforts should include
a determination of the magnitude and areal extent of contamination 1n the
sludges of Taylor Lake, and the removal of the most contaminated materials.
The following recommendations may help focus additional source investiga-
tions in Hylebos Waterway for chlorinated hydrocarbons (i.e., benzenes,
butadienes, and ethenes):
• Analyze the main plant discharges at Occidental and Pennwalt
to better quantify their importance as contaminant sources.
If Occidental is confirmed as an ongoing source of chlorinated
benzenes and butadienes, as suggested herein, then the 1n-plant
sources of these compounds to the waste stream should be
eliminated. This probably would involve replacement of
the graphite anodes currently used.
• Continue monitoring groundwater beneath Occidental, which
is the largest contributor of chlorinated ethenes to Hylebos
Waterway. Evaluate available groundwater treatment technologies
for their potential application on the Occidental property.
7.72
-------
HYLEBOS WATERWAY
• Consider assessing the extent of contamination in sludges
disposed at Taylor Lake at Pennwalt and the feasibility
of removing contaminated material.
• Evaluate resuspension of contaminated sediments directly
off the dock at Occidental when reviewing future dredging
permit applications in the area.
Of the chlorinated hydrocarbons identified to be of concern in Hylebos
Waterway, chlorinated ethenes have the greatest solubility. This suggests
that source controls implemented at Pennwalt would be particularly effective
in improving sediment quality in Hylebos Waterway. Were the sources of
chlorinated ethenes eliminated, a decrease in chlorinated ethene concen-
trations in sediments of the waterway could be expected in a relatively
short period of time. Both the chlorinated benzenes and butadienes are
more persistent than are the chlorinated ethenes. Therefore, sediment
removal, as well as source control, may be necessary for these compounds.
7.2.8 Pentachlorocyclopentane Isomer
7.2.8.1 Spatial Distribution--
The distribution of a pentachlorocylopentane isomer (tentative identifi-
cation) in the surficial sediments of Hylebos Waterway is shown in Figure
7.2.32. This compound is only one of a number of co-existing chlorinated
compounds in Hylebos Waterway sediments. Only a portion of these compounds
has been identified. Highest sediment concentrations of the Isomer, normalized
to dry weight or organic carbon, were found about 4,000 ft from the mouth
of the waterway. Concentrations of the pentachlorocyclopentane isomer
in the surficial sediments were uniformly low less than 3,000 ft from the
mouth and greater than 6,000 ft. The overall pattern of contamination
resembled those shown in Figures 7.2.19 through 7.2.23 for chlorinated
benzenes and chlorinated butadienes, suggesting that a common source may
be involved. No AET was established for this compound.
The vertical pattern of contamination of pentachlorocylopentane could
not be determined because sediment core data were not yet available for
the compound.
7.2.8.2 Loading Estimates--
No known effort has been made specifically to analyze any discharge
to Hylebos Waterway for pentachlorocyclopentane isomers or other cycloalkanes.
7.2.8.3 Source Identificatlon--
The area of greatest sediment contamination by this and other chlorinated
substances was immediately off the main outfall of Occidental Chemical
Corporation. Although neither pentachlorocylopentane or any other chlorinated
cycloalkane is known to occur in the waste stream of Occidental or any
7.73
-------
Segment
260 -
£
cr>
'v
>
"D
-D
a
a
3
5
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V
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220 -
200
180
160 -
1*0 -
120 -
100 -
80 -
60 -
40 -
20 -
0

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0 D _
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5 -
4 -
3 -
2 -
6 8 10 12
(Thousands)
Ft. from mouth of woterwoy
14
16
_DCL
—OyJi—
T
~
O
P-
6
6 10
(Thousands)
Ft. from mouth of waterway
0 Tttrt T«ch Invcitlgitlon - qu*nt1t«ted vilue
Figure 7.2.32
i
12
(A)
AET > 72 ppb
(not established)
~
D d °
r
14
T
~i—
16
(B)
Benthlc
Effects
AET
Toxicity
AET
CONCENTRATIONS OF PENTACHLOROCYCLOPENTANE IN THE SURFICIAL SEDIMENTS OF
THE HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
A) Concentrations on a dry weight basis
B) Concentrations normalized to total organic
carbon content of the sediments
7.74
-------
HYLEBOS WATERWAY
other firm in the tideflats area, the proximity of the Occidental outfall
to the area of contamination suggests strongly that this discharge may
be the ultimate source.
Chlorinated cycloalkanes could be in the Occidental waste stream (Payne,
J., personal communication). The firm produces chlorine by electrolysis
of a sodium chloride brine. Although the firm has partially converted
to steel titanium anodes, graphite anodes impregnated with linseed oil
have historically been used. During electrolysis, the linseed oil reacts
with the free chlorine in the cell, producing a wide variety of chlorinated
organic by-products. Chlorinated organic compounds found in the Occidental
waste stream include chloroform, carbon tetrachloride, chlorinated ethenes,
chlorinated propenes, chlorinated butadienes, chlorinated benzenes, and
several unidentified chlorinated organic compounds (Yake 1980; Riley 1981).
A cyclic structure, such as pentachlorocyclopentane, could be formed if
an alkene undergoes a cycloaddition reaction with another unsaturated molecule
(Roberts et al. 1981). This reaction could be favored by electrolysis
of the brine. While the existing data are inadequate to establish that
pentachlorocylocpentane is formed in the chlorine cells rather than in
other production facilities at Occidental (e.g, the old solvent plant),
the above scenario does provide a reasonable explanation to serve as a
basis for further investigations.
7.2.8.4 Summary and Recommendations--
Since chlorinated cycloalkanes have not typically been contaminants
of concern to regulatory agencies, neither the discharge of Occidental
Chemical Corporation nor those of any other industry in the tideflats area
has been tested for these compounds. Nevertheless, it appears likely that
Occidental Chemical Corporation is the major source of the pentachlorocyclo-
pentane isomers and related cycloalkanes to Hylebos Waterway for a number
of reasons:
• Concentrations of pentachlorocyclopentane were elevated
in the waterway sediments immediately off the main plant
outfall.
• The distribution of the contaminant 1n the sediments was
very similar to the distributions of chlorinated benzenes
and butadienes (Occidental has been shown to be a major
source).
• Pentachlorocylopentane and other cycloalkanes could be formed
1n the chlorine production cells at Occidental.
If pentachl orocyclopentane 1s eventually determined to be a problem
chemical then:
• Groundwater beneath Occidental Chemical Corporation should
be analyzed for the presence of chlorinated cycloalkanes.
7.75
-------
HYLEBOS WATERWAY
• The mass spectra of "unidentified chlorinated organics"
reported to be in the Occidental effluent during the Class
II survey should be reviewed to determine if chlorinated
cyclopentanes are present.
7.2.9 Arsenic
7.2.9.1 Spatial Distribution—
Surficial sediments of Hylebos Waterway contained concentrations of
arsenic ranging from approximately 4 to 700 mg/kg (Figure 7.2.33). This
range was not constant over the length of the waterway. Arsenic concentrations
in surficial sediment were significantly elevated in the upper 6,000 ft
(Segments 1, 2 and 3) relative to the remainder of the waterway. This
spatial distribution indicates sources located near the head of the waterway.
The highest concentrations occurred in Segment 2 at intertidal stations
between 11,500 and 13,000 ft from the mouth, and at the upper end of Segment
1 between 16,000 and 16,500 ft from the mouth. This suggests the presence
of at least two sources in the waterway. As discussed earlier, data normalized
to percent fine-grained material are not presented for arsenic or other
inorganic substances. Grain size data are missing for the intertidal samples
with the highest concentrations.
The four sediment cores taken in upper Hylebos Waterway, approximately
12,000 to 14,000 ft from the mouth, showed different vertical patterns
of arsenic contamination. Arsenic concentrations in the surface horizons
of three cores (HY-60, HY-60A, HY-61) were 4 to 20 times greater than those
in lower horizons. Concentrations in the surface horizon of core HY-60B
were lower than those 1n lower horizons. The vertical pattern of arsenic
contamination suggests that present input of arsenic is generally greater
than historical input.
7.2.9.2 Loading Estimates-
There are 22 discharges to Hylebos Waterway with calculated arsenic
loadings. Arsenic loadings in surface runoff from six log sorting yards
have also been estimated (Norton and Johnson 1985a). Loadings, concentrations,
and flows from each of these sources are shown in Table 7.2.7. The greatest
quantified loadings of arsenic were attributable to discharges from the
Pennwalt Corporation property (14.6 lb/day). Drain HY-056, a presently
disconnected surface water runoff outfall, contributed 7.2 lb/day. The
Pennwalt main outfall effluent contributed 4.3 lb/day. Other surface water
runoff discharges and groundwater seeps at Pennwalt contributed an additional
2.2 lb/day. An additional 0.92 lb/day arsenic 1s contributed by groundwater
beneath the Pennwalt property (not shown 1n Table 7.2.7; AWARE 1981).
Other discharges contributing over 1 lb/day of arsenic to Hvlebos
Waterway Include the Occidental Chemical Corporation's main outfall (4.7
lb/day), the Wasser Winters log sorting yard (4.4 lb/day), the Louisiana
Pacific log sorting yard (4.3 lb/day), Hylebos Creek (2.4 lb/day), and
the Murray Pacific log sorting yard No. 1 (1.4 lb/day).
7.76
-------
Segment
600 -
500 -
400 -
300 -
200 -
100

° <$ yj a

DO
o
rp—g- ¦
_ CO-
dB *
• c
T
T~
• 8 10
(Thousands)
Ft. from mouth of wotcrwoy
T—
12
« #
%
»Dr
14
—1—
16
& "Toxicity AET
Benthlc
Effects
AET
O T»tr« Tech Investlgttlon - quintlttted velue
O Other Investigations - quint It* ted vtlwe
* Other Investigation* - less then vilue
» Other Investigations - undetected vtlue
Figure 7.2.33
CONCENTRATIONS OF ARSENIC IN THE SURFICIAL SEDIMENTS OF
THE HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
Concentrations on a dry weight basis
7.77
-------
Table 7.2.7
ARSENIC: SUMMARY OF LOADINGS FROM DISCHARGES TO HYLEBOS WATERWAY
Drain #
Drain Name
Flow (MGD)
(Avg. and Range)
(I of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(f of Observations)
Loading (lbs/day)
(Avg. and Range)
INDUSTRIAL DISCHARGES

HK-052
Kaiser Ditch
1.9
(0.23-2.9)
(n-8)
6/3/80-4/17/84
41
(4-120)
(n-9)
0.65
(0.063-1.90)
HY-058
Pennmlt Main Outfall
11
(9.4-12)
(n»2)
6/2/81
Not available
3.9 (net)
(n-1)
HT-704
Sound Refining Main
Eff1uent
0.053
(n-I)
6/3/80
3
(nil)
0.0013
DRAINS AND RUNOFF

HM-028
Horningside Ditch
0.66
(0.49-0.78)
(n-3)
9/23/80-11/7/83
8.1
(2-20)
(n-7)
0.0045
(0.0011-0.011)
HY-016
Crack in Bulkhead
0.071
(n-1)
9/24/80
71
(n«l)
0.042
HY-018
Eight-inch Steel Pipe
0.001
(n-1)
6/30/81
15
0.00013
HY-021
Thirty-Inch Concrete
Pipe
0.060
(n-1)
4/28/82
12
(n-1)
0.0060
HY-023
Storm Drain from
hillside NE of
Hlghllne Road
0.050
(n-1)
4/26/62
69
M)
0.037
HY-054
East Channel Ditch
0.0055
(0.0014-0.01)
(n-3)
9/23/80-S/l7/84
14.740
(110-140.000)
(n-6)
0.68
(0.0050-6.4)
HY-055
Eight-Inch PVC Pipe
0.0046
(n-1)
4/7/81-5/31/83
1.318
(770-1,700)
(n-2)
0.051
(0.030-0.065)
HY-056
S1x-1nch Concrete Pipe
(currently disconnected)
0.017
(0.0043-0.029)
(n-2)
4/7/81-8/13/81
50.730
1.920-114.000
(n-4)
7.2
(0.27-16.16)
HY-063
E1ghteen-1nch Steel
Pipe
0.11
(0.012-0.39)
(n-5)
11/4/83-5/3/84
643
(199-1.756)
(n-5)
0.77
(0.18-1.6)
7.78
-------
Table7.2.7(cont'd)
HY-065
Six and E1ghteen-1nch
Steel Pipes
0.039
(0.011-0.11)
(n-4)
11/4/83-5/3/84
2,431
(950-4,776)
(n-5)
0.79
(0.31-1.6)
HY-066
Lincoln Avenue Storm
Drain
0.043
(0.029-0.05)
(n-3)
4/28/82-5/31/84
21
(1-37)
(n-3)
0.00075
(0.00036-0.013)
HY-076
Th1rty-1nch Concrete
Pipe
0.040
(n-1)
4/28/82
31
(n-1)
0.010
HY-078
Twelve-Inch Concrete
Pipe
0.025
(0.02-0.03)
(n*2)
5/17/84
4
(n-1)
0.00083
HY-085
Seven Steel Pipes
0.0007
(n-1)
9/23/80
105
(n-1)
0.00061
HY-70B
Pennwalt East Storm
Drain (currently
disconnected)
0.0043
(n-1)
4/7/81
1,600
(n-1)
0.057
HY-709
Pennwalt Sewer Pipe
(currently discon-
nected)
0.0066
(0.0058-0.0074)
(n-2)
6/3/80-6/2/81
23,000
(7,500-49,000)
(n-3)
1.3
(0.41-2.7)
GROUNDWATER BANK SEEPS

HY-700
Pennwalt East Seep
0.00079
(0.00036 - 0.0014)
(n-3)
6/3/80-4/18/84
113
(36-310)
(n-4)
0.00075
(0.000028-0.0020)
HY-701
Pennwalt West Seep
0.0012
(0.001-0.0014)
(n-2)
9/23/80-8/13/81
11,935
(5,000-25,300)
(n-3)
0.12
(0.050-0.25)
LOG SORT YARDS

Nasser Winters
0.13
(0.015-0.32)
(n-5)
11/4/83-5/3/84
6,400
(1,400-12.000)
(n-5)
4.4
(1.5-10.4)
Hurray Pacific Yard #1
0.20
(0.023-0.73)
(n-5)
11/4/83-5/3/84
1.800
(500-3,400)
(n-5)
1.4
(0.25-3.1)
Cascade Timber Yard #1
0.003
£i)
12/12/83-6/29/84
4,625
(1,970-7,280)
(n-2)
0.12
(0.049-0.18)
Cascade Timber Yard #2
0.035
(0.005-0.065)
(n-2)
12/12/83-6/29/84
2.531
(122-4.940)
(n-2)
0.74
(0.036-1.4)

Louisiana Pacific
0.36
(0.06-0.66)
(n-2)
12/12/83-6/29/84
1,415
(850-1.980)
(n-2)
4.3
(2.6-5.9)
7.79
-------
Table7.2.7(cont'd)
Weyerhaeuser
0.055
(0.024-0.086)
(n-2)
1/5/84-6/29/84
38
(32-44)
(n-2)
0.018
(0.015-0.020)
Ounlap Towing
Not available
12/12/83-6/29/84
3,240
(2,680-3.800)
(n-2)
...
HYLEBOS CREEK

HC-000 Hylebos Creek
WDOE Station 17
16
(4.9-44)
(n«5)
8/22/83-9/5/84
18
(2-67)
(n-12)
2.4
(0.27-6.9)
NOTES: Arsenic has been analyzed for. but not detected 1n the following drains (numbers In parentheses represent numbers of
analyses and detection limits): HY-017 (1, 2 ug/1) and HY-077 (1, 16 ug/1).
No net loading of arsenic ms reported for HY-707 (Occidental main effluent) In the single set of analyses for which
both Influent and effluent data are available (Yake 1980).
L » less than
7.80
-------
HYLEBOS WATERWAY
7.2.9.3 Source Identification--
Based on both sediment chemistry and loading data, Pennwalt Corporation,
log sorting yards, and Hylebos Creek are presently or have been major sources
of arsenic to Hylebos Waterway. These three sources are discussed below.
Pennwalt Corporation—Intertidal sediments along the Pennwalt waterfront
had higher arsenic concentrations than any other surficial sediments in
Hylebos Waterway. Arsenic loading from discharges associated with the
Pennwalt property was approximately three times that from any other source.
Therefore, the firm has probably been a source of arsenic to the waterway.
Of the 14.2 lb/day of arsenic attributable to Pennwalt, over half
(8.5 lb/day) can be attributed to three drains that are currently disconnected:
HY-056, HY-708, and HY-709. Prior to 1981, these drains (and a fourth
unnumbered drain) discharged surface water runoff from the eastern portion
of the plant property, where sodium arsenite pesticide (Penite) had been
produced in the 1940s and 1950s (AWARE 1981; Yake 1982a). Sodium arsenite
sludges were landfilled on the property between the chlorine and sodium
hydroxide production area and the Taylor Lake waste ponds. AWARE (1981)
suggested that arsenic in the effluent from HY-056, HY-708, and HY-709
originated from arsenite sludges remaining in the sewers from the period
of Penite production. In 1981, discharge from these drains was discontinued
and all surface water runoff was routed to the main plant outfall.
The effect on arsenic loading of diverting surface water runoff 1s
not known, because arsenic analyses of this effluent have not been done
since then. Prior to rerouting the runoff from the four eastern drains,
analyses of the main outfall effluent performed during the WDOE Class II
survey indicated a net loading of 3.9 lb/day arsenic to Hylebos Waterway.
The source of the arsenic to the main outfall 1s unknown. No current process
waste stream at Pennwalt is expected to contain arsenic. Any increase
in arsenic concentrations in the main outfall effluent above that measured
in the influent should originate only from surface water runoff.
Groundwater from beneath the Penite sludge disposal area has been
and continues to be a source of arsenic to the waterway. Estimated loadings
from groundwater sources are approximately 0.92 lb/day (AWARE 1981). femedial
action such as capping the Penite pond is being discussed with Pennwalt
at this time, but the potential improvement of groundwater quality cannot
be predicted (Pierce, R., personal communication).
Log Sorting Yards—There are six unpaved or partially paved log sorting
yards along Hylebos Waterway. They include Cascade Timber yards No. 1
and 2, Wasser Winters yard, the Louisiana Pacific yard, Murray Pacific
yard No. 1, and Dunlap Towing. Together, these yards contribute approximately
11 lb/day of arsenic to Hylebos Waterway via surface water runoff. (No
flow data were available from Dunlap Towing to calculate loading.) This
arsenic originates ASARCO slag, which was used as ballast at these yards.
Available information from Norton and Johnson (1985a) indicates that 1,100
7.81
-------
HYLEBOS WATERWAY
tons of slag have been used as ballast at Dunlap Towing and 29,225 tons
have been used at Murray Pacific yard No. 1. Quantities of slag used at
other yards have not been documented. ASARCO slag was not used as ballast
at the Weyerhaeuser log sorting yard. The Weyerhaeuser yard is the only
completely paved yard in the tideflats area and contributes less arsenic
than any other log sorting yards. All or part of the other yards are unpaved.
Norton and Johnson (1985a) sampled yard runoff, nearshore and offshore
sediments, and water near the sorting yards in Hylebos Waterway. The Wasser
Winters yard and Murray Pacific yard No. 1 were sampled more intensively
than the other five yards because most of their runoff is channeled and
thus is more effectively sampled. Arsenic concentrations in runoff from
all seven yards varied considerably, ranging from 32 ug/L at Weyerhaeuser
(January 5, 1984) to 12,000 ug/L at Wasser Winters (May 3, 1984).
Based on the loading data presented earlier, Wasser Winters, Louisiana
Pacific, and Murray Pacific yard No. 1 are the largest contributors of
arsenic to the waterway. Arsenic loading from Dunlap Towing was not quantified,
but its contribution could be greater than either Murray Pacific yard No. 1
or Louisiana Pacific (Norton and Johnson 1985a). The loadings discussed
above and presented in Table 7.2.7 are based on actual measurements of
arsenic concentrations and surface water runoff flow provided by Norton
and Johnson (1985a). Norton and Johnson also estimated loading based on
yard surface area and runoff coefficients. Total estimated average annual
daily loading from the six log sorting yards calculated in this manner
was 2.3 lb/day. Loading during storm events 1s probably higher. As noted
by Norton and Johnson (1985a), the loadings calculated from runoff coefficients
and surface areas are less than those determined by actual measurements,
probably because the former technique may substantially underestimate loading
during storm events.
Groundwater beneath the log sorting yards represents another potential
source of arsenic that has not been quantified. Norton and Johnson (1985a)
estimated that 40 percent of rain falling on the log sorting yards would
leave the properties as surface water runoff. Therefore, approximately
60 percent of precipitation would enter groundwater, with mobilization
of metals as the water migrates through the slag. No data are available
to estimate the magnitude of arsenic input to the waterway via this route.
Hylebos Creek--An arsenic loading of 2.4 lb/day has been calculated
for Hylebos Creek. The W00E assessed sources of arsenic to the creek in
1983 and 1984 (Johnson and Norton 1984a). Low-flow and high-flow surveys
were conducted to focus on changes 1n contaminant loadings with changes
1n surface water runoff conditions. Two major sources of arsenic were
investigated: the U.S. Gypsum landfill adjacent to Interstate Highway
5, and the B&L Landfill on the Surprise Lake tributary to Hylebos Creek.
The U.S. Gypsum landfill was used for disposal of baghouse dust, recovered
from the manufacture of mineral-based insulation. ASARCO slag was used
as a raw material for the insulation. The baghouse dilst 1s known to contain
21.7 percent arsenic by weight. Approximately 10,000 - 15,000 yd3 of solid
wastes were dumped 1n this 2.6-ac landfill between 1971 and 1973 (Dames
and Moore 1983). Off-specification mineral fibers and shot material were
7.82
-------
HYLEBOS WATERWAY
also placed in this landfill and are potential sources of arsenic, although
they contain much less arsenic than does baghouse dust. The landfill has
been inactive since 1979. As of December, 1984, all contaminated material
had been removed from this landfill by U.S. Gypsum. Thus, release of arsenic
from the site to Hylebos Creek can be expected to decrease with time.
B&L Landfill consists primarily of soil and wood wastes from log sorting
yards in the Tacoma tideflats. This site is not a permitted landfill,
operations have apparently ceased, and potential for enforcement action
is being pursued (Hedges, J., personal communication; Pierce, R., personal
communication). The WDOE study (Johnson and Norton 1984a) found that leachate
from this landfill contained up to 10,000 ug/L total arsenic during January,
1982 and as much as 26,900 ug/L in August, 1983. In summer low-flow periods,
leachate from B&L Landfill does not significantly impact arsenic concentrations
in Hylebos Creek. However, in winter high-flow periods, discharge from
the B&L Landfill is the largest source of arsenic to Hylebos Creek and
results in a threefold increase in arsenic concentrations in Hylebos Creek
in the vicinity of the discharge (Johnson and Norton 1984a).
7.2.9.4 Summary and Recommendations--
Based on the spatial gradient of arsenic contamination in surficial
sediments, the major sources of arsenic to Hylebos Waterway are located
in Segments 1 and 2. A number of sources in this area have been identified.
However, it is difficult to prioritize these sources with regard to future
remedial action, since the success of past remedial actions at Pennwalt
and at the US. Gypsum landfill have not been adequately assessed. Four
major sources of arsenic to Hylebos Waterway are summarized below in order
of ascending mass loading:
• Pennwalt Corporation - The total arsenic loading to Hylebos
Waterway from discharges on this property was calculated
to be 14.2 lb/day in the early 1980s. Since 1981, the disconnec-
tion of several discharges and the rerouting of surface
water runoff may have substantially reduced the loading
from this facility. The main plant effluent contributes
3.9 lb/day of this total. Since no known process effluents
contain arsenic, the origin of the 3.9 lb/day is not known.
The only known current source of arsenic is the site where
sodium arsenlte sludges have been landfilled. This site
may also be impacting environmental quality via groundwater
(0.9 lb/day arsenic).
• Log Sorting Yards - Total loading of arsenic via surface
runoff from the seven log sorting yards surrounding Hylebos
Waterway 1s 11 lb/day (based on sample data). The largest
contributors to this loading are Wasser Winters (4.4 lb/day),
Louisiana Pacific (4.3 lb/day) and Murray Pacific yard No. 1
(1.4 lb/day). Migration of arsenic from log sorting yards
to Hylebos Waterway through groundwater could be significant
but cannot be quantified at the present time.
7.83
-------
HYLEBOS WATERWAY
• Hylebos Creek - Arsenic loading to the waterway from Hylebos
Creek was estimated at approximately 2.4 lb/day. There
are two major sources of arsenic to the creek, both of which
result from past landfilling of arsenic-contaminated materials:
B&L Landfill (disposal of soil and wood waste from log sorting
yards); and the U.S. Gypsum landfill (disposal of arsenic-
contaminated baghouse dust). The recent removal of contaminated
material from the U.S. Gypsum landfill can be expected to
reduce the release of arsenic from this site over time.
The following recommendations may help define sources of arsenic to
Hylebos Waterway:
• Investigate and control the unexplained high arsenic concentra-
tions in the Pennwalt main effluent.
• Consider removing Penite wastes on the Pennwalt property
to reduce the arsenic quantities reaching Hylebos Waterway
via groundwater.
§ Consider removing contaminated waste or initiating runoff/
leachate controls in order to reduce the migration of arsenic
from the B&L Landfill.
• Establish a network of groundwater monitoring wells in order
to quantify the amount of arsenic reaching Hylebos Waterway
via groundwater from the log sorting yards.
• Initiate runoff control measures at the log sorting yards.
Current discharges of arsenic to Hylebos Waterway could be dramatically
curtailed by the source control measures Identified above. The three sources
identified (Pennwalt, log sorting yards, Hylebos Creek) contribute 92 percent
of the quantified arsenic loading. A substantial reduction in arsenic
concentrations in these sources can be expected to result in a measurable
Improvement in sediment quality over time.
7.2.10 Copper, Lead and Z1nc
7.2.10.1 Spatial Distribution-
Copper, lead, and zinc have been designated as preliminary contami-
nants of concern in Hylebos Segment 1. Distributions of the contaminants
in the surflclal sediments of Hylebos Waterway are shown 1n Figures 7.2.34 -
7.2.36. For copper and zinc, concentrations decreased from the head to
the mouth of the waterway. Concentration (dry weight) of both metals 1n
Hylebos Segment 6 at the mouth of the waterway are approximately one-fourth
of those In Segment 1 at the head of the waterway. There is also some
evidence of decreasing lead concentration from the head to the mouth of
the waterway, although the gradient 1s not as apparent as those for copper
7.84
-------
Segment, 6_
1.3
1.2
1.1
s
i
t 0.9
/•S
¦5 0.8
S 0.7
| 0.6
0.5
0.4
0.3
0.2
0.1
0

• «

3 «
0 CD
—*-i
0
—£—
o
0
1 1 ? «
^ O 0
~ 0
. ~
i s
„*DO
d:m
~
® n
~ ~ D
O
Benthlc effects
and toxicity
AET
6
, 8 10
(Thousands)
Ft. from mouth of waterway
12
14
16
O Tttri Tech Invettlgitlon • quintltited vilue
O Other Investigation* - quant It* ted value
« Other Investigation} - undetected valve
Figure 7.2.34
CONCENTRATIONS OF COPPER IN THE
HYLEBOS WATERWAY WITH DISTANCE
Concentrations on
SURFICIAL SEDIMENTS OF THE
FROM THE MOUTH OF THE WATERWAY
a dry weight basis
7.85
-------
Segment
600
500
400
300
200 -
100 -
3
556 ppm
6100 ppm
O

—
h
i
1
1
1
1
i
i
i } i n i ¦
«
D 0«
tj) o
h 1 ?-
£ ~ o
0 5
> •
1 r
£
B 8_° °
X
•
T 1 1
o a
~
a
a
no °o c ~
Toxicity
AET
Benthlc
Effects
AET
2 ¦
6 8 10 12
(Thouionds)
Ft. from mouth of wotarwey
14
16
D Tctri Tech Investigation • quintlttted value
O Other Investigations - quint luted value
x Other Investigation* - undetected vilue
Figure 7.2.35
CONCENTRATIONS OF LEAD IN THE SURFICIAL SEDIMENTS OF THE HYLEBOS
WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
Concentrations on a dry weight basis
7.86
-------
Segment
600
500
400 -
300
200 -
100
O 0)
«
I
Do £
B; d
«D
°..~o
c
• ©
c
Oct
> o
D O
1
m ppw.
TTT
P in
&
oD
$
~i 1 1 1 1 1 1 1 1—t
2 4 6 8 10 12
(Thousands)
Ft. from mouth of waterway
I
14
—l—
16
0 Tetri Ttch Investigation • quint1ut«d vtlut
© Other inveitlgttfons • quintltiUd vtlut
Figure 7.2.36
CONCENTRATIONS OF ZINC IN THE SURFICIAL SEDIMENTS OF THE HYLEBOS
WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
Concentrations on a dry weight basis
7.87
-------
HYLEBOS WATERWAY
and zinc. Nickel is a priority contaminant in Segments 2 and 5. Although
source evaluations were not conducted for nickel, it has a similar distribution
to the other metals discussed in this section (Figure 7.2.37).
Superimposed upon the gradients along the length of the waterway are
two areas of elevated concentrations associated with nearby sources. Increased
metal concentrations were apparent in intertidal stations located at 12,000
and 4,000 ft from the waterway mouth. Concentrations of all three metals
were elevated at one or more intertidal stations at 12,000 ft from the
mouth of the waterway. At 4,000 ft from the mouth, lead concentrations
(dry weight) in intertidal sediments were up to three orders of magnitude
greater than those in sediments from nearby stations in the central waterway.
Except for lead, metal concentrations were not significantly elevated at
these stations when normalized to dry weight. Sediments at these stations
were extremely coarse (0.5-1.2 percent fines) and concentrations were high
when normalized to percent fine-grained material.
The intertidal stations at 4,000 and 12,000 ft from the waterway that
had elevated concentrations of one or more of the metals were located along
the southern shoreline, indicating the presence of metal sources along
this shore. Beyond this, there were no cross-waterway gradients of contamina-
tion to help establish locations of other sources.
Sediment core samples taken about 12,000 and 14,000 ft from the mouth
of the waterway showed the same distribution of metals with depth in the
sediments (Figure 7.2.38). Concentrations of all metals were 3 to 10 times
greater in the upper horizon than they were in subsurface horizons. This
indicates the copper, lead, and zinc input to Hylebos Waterway above 12,000
ft from the mouth is substantially greater at present than it was 1n the
past.
7.2.10.2 Loading Estimates--
Oata available for copper, lead and zinc loading to the Hylebos Waterway
are shown in Tables 7.2.8, 7.2.9, and 7.2.10.
On the basis of these data, the major sources of copper to Hylebos
Waterway were the Pennwalt main outfall (2.4 lb/day); Hylebos Creek (2.4
lb/day); the Cascade Timber yard No. 2, Wasser Winters, and Louisiana Pacific
log sorting yards (1.2, 1.0 and 0.73 lb/day, respectively); and Kaiser
Ditch (0.43 lb/day). The greatest sources of lead were Hylebos Creek (1.1
lb/day), Cascade Timber yard No. 2 (0.72 lb/day), Wasser Winters (0.62
lb/day), Kaiser Ditch (0.51 lb/day), and Louisiana Pacific (0.49 lb/day).
The greatest sources of zinc were Hylebos Creek (6.5 lb/day), Kaiser Ditch
(1.8 lb/day), Cascade Timber yard No. 2 (1.6 lb/day), Wasser Winters (1.5
lb/day), and Murray Pacific yard No. 1 (1.5 lb/day). It should be noted
that no flow data were available for Dunlap Towing, although the facility
could be as significant a source of metals as the other log sorting yards
listed (Norton and Johnson 1985a).
7.88
-------
Segment 6
90
80 -
j, 70
!
60 -
i
L 50 -
L
40-
I
I
\
30 -
I 20-
I
10 -
0
3D
CD
+ °
+
o
a *¦
V
*
o
~
~
L —Do
a + ~
t 1 1 1 1—"—i 1 1 r~
4 6 8 10 12
(Thousands)
Ft. from mouth of waterway
1-D
+
+
+
14
"1 1—
16
Berithlc effects
and toxicity
AET
Q Titrt Tech Investigation - quantHettd value
O Other 1nv(tt
-------
(A)
_ 0.2 H
4->
C
I
•¦5 0.4
01
to
Q- 0.6
o>
o
0.8 -
Concentration (ntg/Kg dry weight)'
10 100
1000

1
1
1
1
1
1
1
1
1
1

1
1 :
1 :
i :

JE
4->
| 0.2
•r-
•o
0>
0.4 -
CL
04
O
(B)
Concentration (mg/Kg dry weightf
10 100
x *
T
-L
1000
Figure 7.2.38 (A and B)
CONCENTRATIONS OF HETALS WITH DEPTH IN THE SEDIMENT COLUMN:
(A) STATION HY-60, 601, (B) STATION HY-60A, B01
Copper
Lead
Zinc
No AET are exceeded for these metals
In the cores shown (see Table 4.1 for
AET values).
7.90
-------
-b 0.2
0)
to
g- 0.4
o
^ 0.2
c
•a
oj
t/>
- 0.4
(C)
Concentration (mg/Kg dry weight)3
10 100
I i I

(D)
Concentration (mg/Kg dry weight)
10
100
* i ¦
4-4.
I I I I
1000
¦ ¦ I
u
Zinc bentMc
effects AET
1000
... I
Q.
-------
Table 7.2.8
COPPER: SUMMARY OF LOADINGS FROM DISCHARGES TO HYLEBOS WATERWAY
Drain 1
Drain Name
Flow (MGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(f of Observations)
Loading (lbs/day)
(Avg. and Range)
INDUSTRIAL DISCHARGES

HK-052
Kaiser Ditch
1.9
(0.23-2.9)
(n-8)
6/3/80-11/7/83
27
(15-64)
(n-5)
0.43
(0.24-1.01)
HY-058
Pennwalt Main Outfall
11
(9.4-12)
(n-2)
5/22/79-6/2/81
Not available
2.4 (net)
(1.5-3.3)
(n-2)
HY-704
Sound Refining Main
Eff1uent
0.0S3
(n«l)
6/3/80-6/30/81
13
(3-16)
(n-2)
0.0057
(0.0013-0.00071)
DRAINS AND RUNOFF

HM-028
Horn1ngs1de Ditch
0.66
(0.49-0.78)
(n-3)
9/23/80-11/7/83
20
(10-41)
(n-4)
0.11
(0.055-0.23)
HY-016
Crack In Bulkhead
0.071
(n-1)
9/24/80-6/30/81
21
(14-27)
(«-2)
0.012
(0.0083-0.016)
HY-018
Eight-inch Steel Pipe
0.001
(n-1)
6/30/81
10
(n-1)
0.000083
HY-054
East Channel Ditch
0.00S5
(0.0014-0.01)
(n-3)
9/23/80-5/17/84
9,037
(18-90,000)
(n-5)
0.41
(0.00083-4.1)
HY-055
Eight-inch PVC Pipe
0.0046
(n-D
4/7/81
23
£i)
0.00088
HY-056
Six-inch Concrete Pipe
(currently disconnected)
0.017
(0.0043-0.029)
(n-2)
6/3/80-6/2/81
131
(3-363)
(n-3)
0.019
(0.00043-0.051)
HY-063
Eighteen-Inch Steel
Pipe
0.11
(0.012-0.39)
(n-5)
11/4/83-5/3/84
75
(31-170)
(n-5)
0.069
(0.028-0.16)
HY-065
Six and Elghteen-inch
Steel Pipes
0.039
(0.011-0.11)
(n-4)
11/4/83-5/3/84
367
(224-668)
(n-5)
0.12
(0.073-0.22)
HY-066
Lincoln Avenue Storm
Drain
0.043
(0.029-0.05)
(n-3)
5/17/84-5/31/84
19
(9-28)
(n-2)
0.0068
(0.0032-0.010)
7.92
-------
Table7.2.8(cont'd)
HY-076 Th1rty-1nch Concrete
Pipe
0.040
M)
4/28/82
20
(n-1)
0.0067
HY-078 Twelve-Inch Concrete
Pipe
0.025
(0.02-0.03)
(n-2)
5/17/84-5/31/84
22
(20-25)
(n-2)
0.0046
(0.0042-0.0052)
HY-083 Two Seeps at Occidental
0.0051
(0.0002-0.01)
(n-2)
4/18/84
281
(76-480)
(n-2)
0.012
(0.0032-0.020)
HY-08S Seven Steel Pipes
0.0007
(n-1)
9/23/80-4/18/84
384
(234-533)
(n-2)
0.0022
(0.0014-0.0031)
HY-708 Pennwalt East Storm
Drain (currently
disconnected)
0.0043
(n-1)
4/7/81
16
(n-1)
0.00057
HY-709 Pennwalt Sewer Pipe
(currently discon-
nected)
0.0066
(0.0058-0.0074)
(n-2)
6/3/80-6/2/81
26
(15-50)
(n-3)
0.0014
(0.00083-0.0028)
GROUNDWATER BANK SEEPS

HY-700 Pennwalt East Seep
0.00079
(0.00036-0.0014)
(n-3)
6/3/80-4/18/84
83
(11-160)
(n-4)
0.000547
(0.000072-0.0011)
HY-701 Pennwalt Nest Seep
0.0012
(0.001-0.0014)
(n-2)
9/23/80-6/2/81
53
(31-75)
(n-2)
0.00053
(0.00031-0.00075)
LOG SORT YARDS

Masser Winters
0.13
(0.015-0.32)
(n-5)
11/4/83-5/3/84
1,200
(160-2,800)
(n-5)
1.0
(0.1S-3.5)
Murray Pacific Yard #1
0.20
(0.023-0.73)
(n-5)
11/4/83-5/3/84
210
(84-410)
(n»5)
0.20
(0.03-0.51)
Cascade Timber Yard #1
0.003
(n-1)
12/12/83-6/29/84
422
(148-695)
(n-2)
0.011
(0.0037-0.017)
Cascade Timber Yard #2
0.035
(0.005-0.065)
(«-2)
6/29/84
4.000
M)
1.2
Louisiana Pacific
0.36
(0.06-0.66)
(n-2)
12/12/83-6/29/84
242
(73-410)
(n-2)
0.73
(0.21-1.2)
Meyerhaeuser
0.055
(0.024-0.086)
(n-2)
6/29/84
121
M)
0.056
7.93
-------
Table 7.2.8(cont' d)
Dunlap Towing Not available 12/12/83-6/29/84 263
(183-342)
(n-2)
HYLEBOS CREEK
HC-000 Hylebos Creek 16 8/22/83-9/5/84 18 2.4
HDOE Station 17 (4.9-44) (1-48) (0.13-6.4)
(n-5) (n-9)
NOTE: Copper has been analyzed for, but not detected 1n the following drains (the numbers In parentheses represent number of
analyses and detection limits): HY-021 (1, 10 ug/1), HY-023 (1, 10 ug/1).
7.94
-------
Table 7.2.9
LEAD: SUMMARY OF LOADINGS FROM DISCHARGES TO HYLEBOS WATERWAY
Drain f
Drain Name
Flow (MGD)
(Avg. and Range)
(1 of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(I of Observations)
Loading (lbs/day)
(Avg. and Range)

INDUSTRIAL DISCHARGES

HK-052
Kaiser Ditch
1.9
(0.23-2.9)
(n«8)
6/3/80-4/17/84
32
(5-127)
(n*9)
0.51
(0.079-2.0)
HY-058
Pennwalt Main Outfall
11
(9.4-12)
(n»2)
5/22/79-6/2/81
Not available
0.16 (net)
(0.12-0.19)
(n-2)
HY-704
Sound Refining Main
Effluent
0.053
(n-I)
6/3/80, 6/30/81
19
(17-21)
(n-2)
0.0084
(0.0075-0.0093)
HY-707
Occidental Main Effluent
15.49
(n*l)
9/25/79-10/24/79
Not available
L0.39 (net)
(n-1)
DRAINS AND RUNOFF

HH-028
Mornlngslde Ditch
0.66
(0.49-0.78)
(n-3)
9/23/80-11/7/83
25
(12-73)
(n-6)
0.14
(0.0066-0.40)
HY-016
Crack 1n Bulkhead
0.071
(n-1)
9/24/80
10
(n-1)
0.0059
HY-018
Eight-Inch Steel Pipe
0.001
(n-1)
6/30/81
2
(n-1)
0.000017
HY-054
East Channel Ditch
0.0055
(0.0014-0.01)
(n-3)
9/23/80-5/17/84
6.782
(5-81.000)
(n-6)
0.31
(0.00023-3.7)
HY-055
E1ght-1nch PVC Pipe
0.0046
(n-1)
4/7/81-5/31/83
16
(5-27)
(n-2)
0.00061
(0.00019-0.0010)
HY-056
S1x-1nch Concrete Pipe
(currently disconnected)
0.017
(0.0043-0.029)
(n-2)
6/3/80-4/7/81
85
(13-157)
(«-2)
0.012
(0.0018-0.022)
HY-063
E1ghteen-1nch Steel
Pipe
0.11
(0.012-0.39)
(i»-5)
2/29/83-5/3/84
49
(1-97)
(»»4)
0.045
(0.00092-0.089)
HY-065
Six and E1ghteen-1nch
Steel Pipes
0.039
(0.011-0.11)
(n-4)
11/4/83-5/3/84
377
(164-547)
(n-5)
0.12
(0.053-0.18)
7.95
-------
Table 7.2.9 (cont'd)
HY-066 Lincoln Avenue Storm
Drain
0.043
(0.029-0.05)
(n-3)
5/17/84-5/31/84
18
(15-20)
(n-2)
0.0065
(0.0054-0.0072)
HY-078 Twelve-Inch Concrete
Pipe
0.025
(0.02-0.03)
(n-2)
5/17/84-5/31/84
17
(3-30)
(n-2)
0.0035
(0.00063-0.0063)
HY-083 Two Seeps at Occidental
0.0051
(0.0002-0.01)
(n-2)
4/18/84
169
(30-306)
(n-2)
0.0072
(0.0013-0.013)
HY-085 Seven Steel Pipes
0.0007
(n-1)
9/23/80-4/18/B4
462
(293-630)
(n-2)
0.0027
(0.0017-0.0037)
HY-708 Pennwalt East Storm
Drain (currently
disconnected)
0.0043
(n-1)
4/7/81
20
(n-1)
0.00072
HY-709 Pennwalt Sewer Pipe
(currently discon-
nected}
0.0066
(0.0058-0.0074)
(n-2)
6/3/80
12
(n-1)
0.00066
GROUNDWATER BANK SEEPS

HY-700 Pennwalt East Seep
0.00079
(0.00036-0.0014)
(n-3)
6/3/80-4/18/84
49
(35-79)
(n-4)
0.00032
(0.00023-0.00052)
HY-701 Pennwalt West Seep
0.0012
(0.001-0.0014)
(n-2)
9/23/80-6/2/81
96
(87-105)
(n-2)
0.00096
(0.00087-0.0011)
LOG SORT YARDS

Nasser Winters
0.13
(0.015-0.32)
(n-5)
11/4/83-5/3/84
700
(130-1,600)
(n-5)
0.62
(0.10-2.0)
Hurray Pacific Yard #1
0.20
(0.023-0.73)
(n-5)
12/29/83-5/3/84
250
(67-350)
(n-4)
0.19
(0.051-0.41)
Cascade Timber Yard 11
0.0034
(H-I)
12/12/83-6/29/84
373
(36-710)
(n-2)
0.0092
(0.00090-0.018)
Cascade Timber Yard #2
0.035*
(0.005-0.065)
(n-2)
6/29/84
2,470
(n-1)
0.72
Louisiana Pacific
0.36
(0.06-0.66)
(n-2)
12/12/83, 6/29/84
164
(17-310)
(n-2)
0.49
(0.051-0.93)
Meyerhaeuser
0.055
(0.024-0.086)
(n-2)
6/29/84
35
M>
0.016
7.96
-------
Table7.2.9 (cont'd)
Dunlap Towing
Not available
12/12/83-6/29/84
219
(171-267)
<«•*)
HYLEBOS CREEK
HC-000
ftylebos Creek
MDOE Station 17
16
(4.9-44)
(n-5)
8/22/83-9/5/84
80
(1-12)
Cn-9)
1.1
(0.13-1.6)
NOTE: Lead has been analyzed for but not detected In the following drains (numbers 1n parentheses represent numbers of
analyses and detection limits): HY-076 (1, 20 ug/1). HY-077 (1, 1 ug/1), HY-021 (1, 20 ug/1), HY-023 (1, 20 ug/1).
4 Flow of Individual discharge only; total yard flow not determined.
7.97
-------
Table 7.2,10
ZINC: SUMMARY OF LOADINGS FROM DISCHARGES TO HYLEBOS WATERWAY
Drain I
Drain Name
Flow (MGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)
INDUSTRIAL
DISCHARGES

HK-052
Kaiser Ditch
1.9
(0.23-2.9)
(n»8)
6/3/80-4/17/84
112
(8-719)
(n-9)
1.8
(0.13-11)
HY-058
Pennwalt Main Outfall
11
(9.4-12)
(n-2)
6/2/81
Not available
0.4 (net)
(n-1)
HY-704
Sound Refining Main
Effluent
0.053
(n-1)
6/3/80-6/30/81
73
(35-90)
(n-2)
0.032
(0.015-0.040)
HY-707
Occidental Main Effluent
15.49
(n-1)
9/25/79
Not available
0.25 (net)
(n-1)
DRAINS AND RUNOFF

HM-028
Mornings1de Ditch
0.66
(0.49-0.78)
(n-3)
9/23/80-11/7/83
176
(51-450)
(n-5)
0.97
(0.26-2.5)
HY-016
Crack in Bulkhead
0.071
(n-1)
9/23/80-11/7/83
L20
(n-1)
L0.012
HY-017
Twelve-Inch Corrugated
Steel Pipe
0.0039
6/30/81
67
(n-1)
0.0022
HY-018
Eight-Inch Steel Pipe
0.001
£l)
6/30/81
170
(^1)
0.0014
HV-021
Th1rty-1nch Concrete
Pipe
0.06
(n-1)
4/28/82
10
(n-1)
0.0050
HV-054
East Channel Ditch
0.0055
(0.0014-0.01)
(n-3)
9/23/80-5/17/84
12,108
(5-120,000)
(n-5)
0.56
(0.000092-5.5)
HY-055
Eight-inch PVC Pipe
0.0046
(n-1)
4/7/81
52
(n-1)
0.0020
HY-0S6
Six-Inch Concrete Pipe
(currently disconnected)
0.017
(0.0043-0.029)
(«-2)
6/3/80-4/7/81
40
(20-60)
(n-2)
0.0057
(0.0028-0.0085)
7.98
-------
Table7.2.10(cont'd)
HY-063
E1ghteen-1nch Steel Pipe
0.11
(0.012-0.39)
(n-5)
11/4/83-5/3/84
433
(136-960)
(n-5)
0.40
(0.12-1.88)
HY-065
Six and Eighteen-Inch
Steel Pipes
0.039
(0.011-0.11)
(n-4)
11/4/83-5/3/84
2 547
(946-4,630)
(n-5)
0.83
(0.31-1.5)
HY-066
Lincoln Avenue Storm
Drain
0.043
(0.029-0.05)
(n-3)
4/28/82-5/31/84
79
(16-127)
(n-3)
0.028
(0.0057-0.046)
HY-076
Thirty-Inch Concrete
Pipe
0.040
(n-1)
4/28/82
72
(n-1)
0.024
HY-078
Twelve-Inch Concrete
Pipe
0.025
(0.02-0.03)
(n-2)
5/17/84
35
(n-1)
0.0073
HY-083
Two Seeps at Occidental
0.0051
(0.0002-0.01)
(n-2)
4/18/84
129
(7-243)
(n-2)
0.0055
(0.00030-0.010)
HY-085
Seven Steel Pipes
0.0007
(n-1)
9/23/80-4/18/84
920
(289-1,550)
(n-2)
0.0054
(0.0017-0.0090)
HY-708
Pennwalt East Storm
Drain (currently
disconnected)
0.0043
(n-1)
4/7/81
615
(n-1)
0.022
HY-709
Pennwalt Sewer Pipe
(currently discon-
nected)
0.0066
(0.0058-0.0074)
(n-2)
6/3/80-6/2/81
35
(20-60)
(n-3)
0.0019
(0.0011-0.0033)
GROUNDWATER BANK SEEPS

HY-700
Pennwalt East Seep
0.00079
(0.00036-0.0014)
(n«3)
6/3/80-4/18/84
106
(2-490)
(n-5)
0.00070
(0.000013-0.0032)
HY-701
Pennwalt West Seep
0.0012
(0.001-0.0014)
(«-2)
9/23/80-6/2/81
240
(80-400)
(n-2)
0.0024
(0.00080-0.0040)
LOG SORT YARDS

Wasser Winters
0.13
(0.015-0.32)
(n-5)
11/4/83-5/3/84
1,800
(490-3,200)
(n-5)
1.5
(0.21-4.0)
Murray Pacific Yard 11
0.20
(0.023-0.73)
(n-5)
11/4/83-5/3/84
1,800
(500-3,400)
(n-5)
1.5
(0.23-3.7)
Cascade Timber Yard #1
0.003
(n-1)
12/12/83-6/29/84
(1,685-3^000)
(n-2)
0.059
(0.042-0.075)
7.99
-------
Table7.2.10(cont'd)
Cascade Timber Yard #2
0.03S
(0.005-0.065)
(n«2)
6/29/84
5,340
(n-1)
1.6
Louisiana Pacific
0.36
(0.06-0.66)
(n-2)
12/12/83-6/29/84
335
(170-500)
(n-2)
1.0
(0.51-1.5)
Weyerhaeuser
0.055
(0.024-0.086)
(n-2)
1/5/84-6/29/84
445
(240-650)
(n-2)
0.2
(0.11-0.3)
Dunlap Towing
Not available
12/12/83-6/29/84
870
(315-1,425)
(n-2)
—
HYLEBOS CREEK

HC-000 Kyiebos Creek
WDOE Station 17
16
(4.9-44)
(n-15)
8/22/83-9/5/84
49
(1-273)
(n-13)
6.5
(0.13-36.4)
7.100
-------
HYLEBOS WATERWAY
Loading estimates indicate that Hylebos Creek is the largest source
of copper, lead, and zinc to Hylebos Waterway. This source is discussed
further in Section 7.2.9.3.
The log sorting yards represent a significant source of copper, lead,
and zinc to the waterway and is further explored below. The Kaiser Ditch
represents another source. This ditch drains not only the Kaiser property,
but also Cascade Timber yard No. 2, Weyerhaeuser, and Dunlap Towing log
sorting yards. The log sorting yards probably contribute a significant
portion of the total loading of metals from the ditch. It should be noted
that the loading values shown herein for the log sorting yards are based
on actual measurements of flow and concentration from the individual yards
during storm events, rather than on the average annual daily loading values
estimated by Norton and Johnson (1985a) using runoff coefficients and yard
area.
While there are no NPDES-permitted discharges of copper or zinc to
Hylebos Waterway, there are two permitted discharges of lead. Pennwalt
Chemical Corporation has an NPDES permit to discharge an average of 1.0 lb/day
(2.0 lb/day maximum). The most recent loading estimate available in the
project database (Yake 1982a) indicated an average net loading of 0.16
lb/day of lead to the waterway. Available Discharge Monitoring Report
(DMR) data indicate that in 1983-1984, Pennwalt Corporation had an average
net loading of approximately 0.6 lb/day lead. Occidental Chemical Corporation
is permitted under the NPDES program to discharge a net average of 2.1
lb/day lead (4.3 lb/day maximum) to Hylebos Waterway. DMR data for 1983-1984
indicate that Occidental had an average net lead loading of 1.7 lb/day.
7.2.10.3 Source Identification-
Sources of copper, lead, and zinc to upper Hylebos Waterway include
permitted process effluents, surface water runoff, and groundwater seepage.
Based on surficial sediment chemistry and loading data, major sources of
metals include Hylebos Creek, the log sorting yards, and the Pennwalt Corpora-
tion main effluent. Based on the elevated lead concentrations in intertidal
sediments at 4,000 ft from the waterway mouth, Occidental Chemical Corporation
is also a past and/or present source of lead to Hylebos Waterway. However,
it is not a source of lead to the head of the waterway where the contaminant
has been designated to be of concern.
Hylebos Creek--Hylebos Creek can be implicated as a major source of
metals on the basis of the gradient of decreasing metal concentrations
in surficial sediments from the head to the mouth of Hylebos Waterway.
Loading data also indicate it is a major source. Hylebos Creek had higher
quantified loadings of lead (1.1 lb/day) and zinc (6.5 lb/day) than any
other discharge to Hylebos Waterway. Hylebos Creek and the Pennwalt Corporation
main outfall had the highest loadings of copper (both 2.4 lb/day).
The data of Johnson and Norton (1985a) indicate that a major source
of metals to Hylebos Creek drainage is the Fife ditch system, entering
the creek about Marine View Drive (1,400 ft upstream from the mouth of
7.101
-------
HYLEBOS WATERWAY
the creek). Flows from this discharge ranged from 0.08 to 10.0 MGD during
WDOE's study (Johnson and Norton 1985a). Copper concentrations were 36
ug/L, lead concentrations were 14 ug/L, and zinc concentrations were 18-54
ug/L. Particularly in wet weather, this storm drainage system could represent
a significant loading. Zinc loading from Fife Ditch to Hylebos Creek during
wet weather was estimated to be 4.7 lb/day (copper and lead data unavail-
able). The source of metals to this discharge is unknown and requires
further investigation.
Two additional potential sources of metals to Hylebos Creek have been
identified and investigated by WDOE (Johnson and Norton 1985a): U.S. Gypsum
landfill and B&L landfill. The U.S. Gypsum Landfill was used to dimp baghouse
dust from the manufacture of insulation made with ASARCO slag. This dust
contains 6.35 percent lead, 2.83 percent zinc, and 1.03 percent copper
by weight. The data of Johnson and Norton (1985a) indicate that U.S. Gypsum
is not a major source of copper, zinc, or lead to Hylebos Creek. U.S. Gypsun
completed excavation and removal of the contaminated portions of the landfill
in December, 1984. Sampling is underway to identify areas of residual
contamination and to determine loading to the Hylebos drainage. Results
were not available at the time of this writing. As a result of the removal
of material from this landfill, input of metals from this source should
decrease still further with time.
The B&L Landfill, about 17 ac in size, has received soil and wood
waste from log sorting yards since about 1975. This site has never been
a permitted or monitored landfill. Discussions have been initiated at
county and state levels to determine an appropriate course of action, but
no remedial action has yet been undertaken (Pierce, R., personal communication;
Hedges, J., personal communication). A sample of leachate from the B&L
Landfill taken in 1982 showed detectable levels of zinc (390 ug/L). Lead
and copper were undetected at 20 ug/L. When resampled in August, 1983,
B&L leachate contained 93 ug/L copper, 115 ug/L lead, and 673 ug/L zinc
(Johnson and Norton 1985a). Based on these data, B&L Landfill appears
not to be a major source of copper, lead, or zinc to Hylebos Creek. During
low-flow conditions, the loading in Surprise Lake drain, into which runoff
from B&L discharges, was below 0.04 lb/day for each metal. During high-
flow conditions, zinc loading was estimated to be 0.24 lb/day. Data for
copper and lead are unavailable from the high flow survey.
Log Sorting Yards--There are seven log sorting yards that drain into
the upper portion of Hylebos Waterway. Together, their runoff contributes
42 percent of the quantified lead loading to the waterway, 35 percent of
the copper loading, and 34 percent of the zinc loading. Among the seven
log sorting yards, Cascade Timber yard No. 2 and Wasser Winters had the
greatest loadings of copper, lead, and zinc. Weyerhaeuser had the lowest
metal loadings. U.S. EPA chronic water quality criteria for the protection
of saltwater aquatic life have been exceeded for zinc in Hylebos Waterway
adjacent to the Murray Pacific yard No. 1 discharge. Corresponding acute
criteria have been exceeded for copper off discharges from Wasser Winters,
Murray Pacific yard No. 1, and at other sites throughout Hylebos Waterway
(Norton and Johnson 1985a).
7.102
-------
HYLEBOS WATERWAY
Log sorting yards along Hylebos Waterway have used ASARCO slag as
ballast. This slag typically contains about 5,000 mg/kg each of lead and
copper, and 18,000 mg/kg zinc (State of Washington Discharge Permit Application,
1971, ASARCO). Relative leaching rates for these compounds from the ballast
are not known. Experiments conducted by Johnson et al. (1982) on slow-cooled
and granulated slags from smelters indicated that cooling rate determines
the leachability of particles within the slag, while particle size and
shape determine the surface area available for leaching. In addition,
the oxidative state of the slag as it cooled is a factor in determining
complexation reactions, again potentially changing their relative leachability.
Finally, the pH of the water to which the slag is exposed will determine
the amount and relative leachability of each metal. The log sorting yard
environment with relatively low pH enhances the leaching of these metals
from slag. The variability in ratios of copper to lead, zinc to lead,
and zinc to copper concentrations in surface runoff from the log sorting
yards reported by Norton and Johnson (1985a) may indicate differences in
type and particle size of slag used, time of slag deposition (composition
may have changed over the years), and pH and redox conditions at each yard.
The extent of groundwater migration of copper, lead, and zinc from
the log sorting yards has not yet been assessed, although it could be sig-
nificant. Among the log sorting yards, the paved yard of Weyerhaeuser
would be expected to have the least groundwater contamination because ASARCO
slag was not used as ballast at this site and the yard has been paved,
preventing infiltration of surface water.
Pennwalt Corporation—The loading data indicate that Pennwalt Corporation
is the major source of copper and a lesser source of zinc and lead. The
surficial chemistry data indicated elevated levels of copper, lead, and
to a lesser extent, zinc, in intertidal stations along the Pennwalt waterfront.
The firm has an NPDES permit to discharge lead. It is unclear why the
effluent concentrations of other metals would be higher than influent concen-
trations.
Kaiser Aluminum and Chemical Company--CH2M HILL (1983) conducted a
water management study for Kaiser Aluminim and Chemical Company to determine
loadings of various contaminants in the storm sewer system on the Kaiser
property. Copper and zinc were present in various locations on the property
in concentrations ranging from <0.02 to 5.3 mg/L and <0.02 to 0.57 mg/L,
respectively. Loadings in Kaiser Ditch just north of the facility parking
lot were calculated at 0.20 lb/day copper and <0.20 lb/day zinc. The presence
of these contaminants may be partially due to atmospheric fallout of particu-
lates from the stack at Kaiser, although there are no available sampling
data to quantify this. A single set of replicate analyses of sludge from
the wet scrubber operations (Kaiser 1983) showed copper at 59 to 110 mg/kg.
lead at 6 to 13 mg/kg, and zinc at 11 to 19 mg/kg, all on a wet-weight
basis and thus not directly comparable to other data. However, the pH
in the sludge ponds (>7) would render the metals relatively insoluble and
limit their mobilization and migration into surface waters or groundwater.
Loading data from Kaiser Ditch show it to be a significant source of metals
7.103
-------
HYLEBOS WATERWAY
to the waterway. However, the portion of the metal loading in Kaiser Ditch
contributed by Kaiser Aluminum is not known. Cascade Timber Yard No. 2,
Dunlap Towing, and Weyerhaeuser log sorting yards drain into or are immediately
adjacent to the Kaiser Ditch and would contribute to the metal loading
of this ditch.
General Metals--The General Metals scrap yard occupies 2,000 ft of
the waterfront on the north shore of upper Hylebos Waterway. Due to the
activities of storing, moving, and crushing metal, the firm is a potential
source of metals. In addition, a portion of this site was used between
1972 and 1977 for the disposal of Occidental Chemical Corporation sludge
pond wastes (Boys and Sceva 1979). The brine sludges making up this waste
result from the sodium chloride purification process and contain up to
450 mg/kg lead and up to 30 mg/kg copper (Feller 1981). Therefore both
surface water and groundwater discharge may be contributing metals to the
waterway.
Tacoma Boatbuilding--Tacoma Boatbuilding is located on the north shore
of the waterway adjacent to General Metals. Though sample density is inadequate
for definitive conclusions, the greatest concentration of copper measured
in Hylebos Waterway during the Tetra Tech survey, and the second highest
concentration of zinc measured, were from a station along the north shore
of the waterway adjacent to Tacoma Boatbuilding. Metal finishing and painting
activities may result in metal contamination of the waterway from sandblasting
grit containing a variety of metals and from antifouling paint containing
copper or other metals. In a recent WD0E inspection of Tacoma Boatbuilding
(circa 1983-84) discharge containing metal plating wastes was observed
entering the Hylebos Waterway (Pierce, R., 15 July 1985, personal communica-
tion). Sandblasting materials have been used by Tacoma Boatbuilding during
the decade they have occupied this site and their disposition have not
been established.
7.2.10.4 Summary and Recommendations--
The spatial gradient of copper, lead, and zinc contamination in surficial
sediments of Hylebos Waterway suggests the presence of multiple sources
in the upper 7,000 ft of the waterway. Benthic and toxicity AET are only
exceeded for these metals 1n inertidal sediments. Four sources have been
found to account for most of the metal input to the upper waterway. All
these sources are ongoing. These are listed below in order of the total
copper, lead, and zinc loading of the discharge:
• Log Sorting Yards - Seven logging sort yards surround upper
Hylebos Waterway. As a group, they contribute at least
11 lb/day metals (sum of copper, lead, and zinc) via surface
water runoff. Additional loading via groundwater could
be significant but is unquantified.
t Hylebos Creek - This discharge contributes 10 lb/day of
metals to Hylebos Waterway. The greatest single contributor
to this loading is Fife ditch, which joins the creek approxi-
7.104
-------
HYLEBOS WATERWAY
mately 1,400 ft upstream from its mouth. The sources of
metals to Fife ditch have not been investigated.
a Pennwalt Corporation - The various discharges from the facility
contribute 4.3 lb/day of metals to Hylebos Waterway. The
majority of this loading is attributable to the main outfall
effuent (3 lb/day). The discharge is permitted through
the NPDES program to discharge an average of 1 lb/day lead,
and past discharges have been within the limit. It is not
clear why the discharge contains significant quantities
of copper and zinc.
• Kaiser Ditch - This discharge contributes 2.7 lb/day of
copper, lead, and zinc combined to Hylebos Waterway. Available
data are insufficient to establish if Kaiser Aluminum or
the log sorting yards bordering the ditch bear the greater
responsibility for the calculated loading.
The following recommendations may help define other sources of copper,
lead, and zinc:
• Sample water and sediment within the drainage area served
by Fife ditch to determine the source of metals in this
discharge. Implement remedial actions, if feasible.
• Sample process and cooling water within the Pennwalt plant
to determine the source of metals observed in the main dis-
charge.
• Survey all discharges to Kaiser Ditch simultaneously to
determine the source of metals.
• Pave or otherwise divert surface water runoff at the log
sorting yards to reduce copper, lead, and zinc migration.
Investigate migration of metals from these sites via ground-
water.
0 Sample of nearshore sediments and surface water runoff in
the vicinity of General Metals and Tacoma Boatbuilding to
establish whether these industries are sources of metals
to Hylebos Waterway.
The four sources identified above contribute approximately 90 percent of
the quantified loading of metals (copper, lead, zinc) to Hylebos Waterway.
Reduction in metal input from these sources should result in a significant
improvement in sediment quality. However, there are insufficient data
on sediment transport, deposition, and mixing rates 1n Hylebos Waterway
to predict the rate at which the recovery will proceed.
7.105
-------
HYLEBOS WATERWAY
7.2.11 Mercury
7.2.11.1 Spatial Distribution--
The spatial gradient of mercury concentrations in surficial sediments
of Hylebos Waterway are shown in Figure 7.2.39. Concentrations ranged
from 0.05 to 1.0 mg/kg (dry weight), with two exceptions. The concentration
of mercury exceeded 3 mg/kg dry weight at Tetra Tech Station HY-40, about
4,700 ft from the mouth of the waterway (Segment 5) and exceeded 15 mg/kg
dry weight in intertidal sediments about 11,000 ft from the mouth of the
waterway (Segment 2). Smaller mercury elevations in Segment 2 were found
at two intertidal stations off Pennwalt, sampled in the Class II survey
(Johnson and Prescott 1982), and two mid-waterway stations at 10,910 ft
from the mouth sampled by Mai ins et al. (1980).
Sediment core data available for mercury in the Segment 5 problem
area are limited to subtidal sediments from cores HY-63, HY-63A, HY-63B,
and HY-63C. These cores are about 1,000 ft closer to the mouth of the
waterway than Station HY-40 where elevated mercury concentrations were
observed, and are directly off the docks at Occidental. Mercury concentrations
decreased with depth in HY-63A, B01, from 0.38 mg/kg in the surface horizon
to 0.14 mg/kg in the lowest horizon. Mercury concentrations increased
with depth in HY-63, G01 (0.42-0.90 mg/kg), HY-63B, B03 (0.20-0.36 mg/kg)
and HY-63C, B05 (0.21-0.50 mg/kg). There was no evidence in these cores
or other Hylebos Waterway cores of the high levels of mercury observed
primarily in intertidal sediments.
7.2.11.2 Loading Estimates-
Mercury has been measured in 20 ditches, drains, and seeps on Hylebos
Waterway (Table 7.2.11). Loading from most of these sources ranged from
0.0001 to 0.001 lb/day. There has been no chemical analysis for mercury
in drains HY-079 to HY-083, within 1,000 ft of the area of elevated sediments.
Mercury measured in the 11th Street bridge storm drain (HY-078) had an
average loading of only 0.000065 lb/day, not nearly enough to account for
the elevation seen at Station HY-40 in the central part of the waterway.
The mercury concentration in the drain at the northwest end of the Occidental
property (HY-085) was 5 ug/L, with a corresponding loading of 0.000029 lb/day
(Osborne 1980b).
7.2.11.3 Source Identification-
Only one potential source of mercury to Hylebos Waterway has been
identified. According to Dames and Moore (1982), Mutual Fir Column, in
business from 1921 to 1974, discharged methylmercuric phosphate through
a sump on their property to a shallow bog in the 1950s. This company,
which made porch columns, was located across the street from Buffelen
Wood-working (Golocci, C., personal communication). J. Guizzetti (personal
communication), of Buffelen Woodworking, does not recall that Mutual Fir
Column treated their poles with methylmercuric phosphate or any other chemical.
In addition, no mention in the literature could be found regarding use
7.106
-------
Segment
3 -
2.8 -
2.6 -
2.4 -
2.2 -
2
1.8 -
1.6 -
1.4
1.2 i
1
0.8 A
0.6
0.4 -
0.2 -
0
3D m
¦X .
CO 0
© D£°«
O o rO «*> D
D O rp n
qD 0
1

n O D
D a
£ «
I l
2
* 15 ppm
T
DD >Pf
X ff
6 8 10
(Thousands)
Ft. from mouth of watsrway
T
12
T
°0 «
hi.
i
14
-A
16
O ttU» Tech Hvtitlgitfon • qumtUtttd vtlut
O Other Investigations • quantluted value
x Other Investigations - undetected vtlue
Figure 7.2.39
CONCENTRATIONS OF MERCURY IN THE SURFICIAL SEDIMENTS OF THE
HYLEBOS WATERWAY WITH DISTANCE FROM THE MOUTH OF THE WATERWAY
Concentrations on a dry weight basis
7.107
-------
Table 7.2.11
MERCURY: SUMMARY OF LOADINGS FROM DISCHARGES TO HYLEBOS WATERWAY
Drain I
Drain Name
Flow (MGD)
(Avg. and Range)
(I of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)
INDUSTRIAL
DISCHARGES

HK-052
Kaiser Ditch
1.9
(0.23-2.9)
(n-8)
9/23/80-4/17/84
0.36
(0.05-1)
(n-7)
0.0057
(0.00079-0.016)
HY-058
Pennwalt Main Outfall
11
(9.4-12)
Cn-2)
6/3/80-6/2/SI
0.30
(n«2)
0.28
HY-704
Sound Refining Main
Effluent
0.053
(n»l)
6/3/80-6/30/81
0.50
(0.080-0.83)
(n-2)
0.00022
(0.000035-0.00037)
DRAINS AND RUNOFF

HM-028
Mornlngside Ditch
0.66
(0.49-0.78)
(n-3)
9/23/80-11/7/83
0.24
(0.07-0.49)
(n-4)
0.0013
(0.00039-0.0027)
HY-016
Crack 1n Bulkhead
0.071
(n-1)
9/24/80-6/30/81
0.15
(0.080-0.21)
(n-2)
0.000089
(0.000047-0.00012)
HY-017
Twelve-Inch Corrugated
Steel Pipe
0.0039
(n-1)
6/30/81
0.17
£l)
0.0000055
HY-018
Eight-Inch Steel Pipe
0.001
(n-1)
6/30/81
0.29
(n-1)
0.000002
HY-019
Twenty-four-1nch
Corrugated Steel Pipe
0.026
(n-1)
6/30/81
,0.17
(n-1)
0.000037
HY-023
E1ghteen-1nch Concrete
Pipe
0.050
(n-1)
4/28/82
0.26
(n-1)
0.00011
HY-054
East Channel Ditch
0.0055
(0.0014-0.01)
(n-3)
9/23/80-5/17/84
3.6
(0.14-11)
(n-5)
0.00017
(0.000006-0.00051)
HY-055
Eight-inch PVC Pipe
0.0046
(n-1)
4/7/81-5/31/83
2.9
(0.8-5)
(n-2)
0.00011
(0.000031-0.00019)
HY-056
S1x-1nch Concrete Pipe
(currently disconnected)
0.017
(0.0043-0.029)
(n-2)
6/3/80-6/2/81
12
(0.60-29)
(n-3)
0.0017
(0.000085-0.0041)
7.108
-------
Tat>le7.2.11(cont'd)
HV-066
Lincoln Avenue Storm
Drain
0.043
(0.029-0.05)
(n«3)
5/31/84
0.34
(n-1)
0.00012
HY-078
Twelve-inch Concrete
Pipe
0.025
(0.02-0.03)
(n-2)
5/31/84
0.31
(n-1)
0.000065
HY-085
Seven Steel Pipes
0.0007
(n-1)
9/23/80
5
(n-1)
0.000029
HY-708
Pennwalt East Storm
Drain (currently
disconnected)
0.0043
(n-1)
4/7/81
6.3
(n-1)
0.00023
MY-709
Pennwalt Sewer Pipe
(currently discon-
nected)
0.0066
(0.0058-0.0074)
(n-2)
6/3/80-6/2/81
5.8
(0.38-16)
(n-3)
0.00032
(0.000021-0.00088)
GROUNDWATER
BANK SEEPS

HY-700
Pennwalt East Seep
0.00079
(0.00036-0.0014)
(n-3)
6/3/80-4/18/84
6.9
(2-12)
(n-4)
0.000045
(0.000013-0.000079)
HY-701
Pennwalt Uest Seep
0.0012
(0.001-0.0014)
(n-2)
9/23/80-6/2/81
9.5
(3-161
(n-2)
0.000096
HYLEBOS CREEK

HC-000
ttylebos Creek
WDOE Station 17
16
(4.9-44)
(n-5)
11/8/83-9/5/84
0.15
(0.051-0.330)
(n«4)
0.020
(0.0068-0.044)
NOTE: Mercury has been analyzed for but not detected 1n the following drains (numbers In parentheses represent numbers of
analyses and detection limits): HY-077 (1, 0.2 ug/1); HY-707 (5, 0.2 ug/1).
7.109
-------
HYLEBOS WATERWAY
of methylmercuric phosphate for wood treating (Sax 1984; Hawley 1981).
In any case, the only probable route of contamination from this source
would be through groundwater seepage. The distance from this property
to the area of elevated mercury concentration makes this a doubtful source,
particularly since elevated mercury concentrations were restricted to an
isolated site in the central waterway.
Historical industrial processes at Occidental Chemical were investigated
to determine whether they had ever used a mercury cell process in chlorine
manufacture. According to F. Monahan (personal communication), the company
has never used this process. Similarly, the elevated concentrations of
mercury in intertidal sediments off Pennwalt Corporation are not known
to be a result of industrial processes. Other possibly unknown historical
activities at this site may be responsible for this contamination.
7.2.11.4 Summary and Recommendations
Sources of mercury were not obvious on the basis of gradients or patterns
of contamination. Elevated mercury concentrations in Segment 5 occurred
at a single station only (Station HY-40). Potential sources are unknown.
In Segment 2, some mercury may be entering the waterway from Pennwalt
Corporation property; however, the origin of this contaminant is not known.
The source of mercury at Pennwalt should be investigated and source
control should be implemented if feasible.
7.2.12 Hylebos Waterway: Summary and Recommendations
7.2.12.1 Summary--
Results of the source identification efforts in Hylebos Waterway are
summarized in Figure 7.2.40. Nine contaminants or contaminant groups were
designated to be of concern in Hylebos Waterway. One or more sources could
be identified with a high degree of certainty for the chlorinated hydrocarbons,
aromatic hydrocarbons, and metals. PCB sources in Hylebos Waterway could
not be clearly identified as historical or ongoing. Exposure of historically
contaminated sediments may be contributing to the patchy distribution of
PCBs in Hylebos Waterway. The spatial gradient of contamination for the
pentachlorocylcopentane isomer clearly implicates a specific source (i.e.,
Occidental Chemical Corporation). This source probably contributes a large
number of chlorinated compounds with covarying concentrations in Hylebos
Waterway sediments. Only some of these compounds have been identified.
Occidental Chemical Corporation is implicated as the major source
of chlorinated hydrocarbons (i.e., chlorinated benzenes, butadienes, and
ethenes) to Hylebos Waterway. Historically, the chlorinated organic compounds
entered the waterway via direct discharge from the chlorine production
facilities and the solvents plant, and via groundwater from spills and
on-site waste disposal. At present, the chlorinated benzenes and butadienes
enter the waterway principally through the main plant outfall. Chlorinated
ethenes presently enter the waterway principally through groundwater and,
7.110
-------
HYIEBOS CREEK
Source of metals
WASSER WINTERS
Source of metals
CASCADE #1
Source of metals
TtCOlM
Boatbuilding
Gan«r»l Metela
I ne
Upper
Turning
Butt
Lower
Turning
Balin
%
| SEGMENT 1 |
SEGMENT
EGMENT 2
U.S.
Gyptum
Taylor Way
MURRAY PACIFIC YARD #1
SEGMENT S
Source of metals
KonnevWe
PENNWALT CORP.
Source of chlorinated ethenes
and metals
Port of
Tacom
Industrial
Yard
CASCADE TIMBER #2
Source of metals
Alcxoitdrr Avcnu*
OCCIDENTAL CHEMICAL CORP.
Source of chlorinated hydrocarbons
(except PCB's)
500 1000
I FEET
LEGEND:
OUNLAP TOWING
Source of metals
! KNOWN OR PR08A8LE SOURCE
KAISER ALUM, & CHEM. CORP.
Source of HPAH
LOUISIANA PACIFIC
Source of metals
Figure 7.2.40
SOURCES OF CONTAMINANTS TO THE
HYLEBOS WATERWAY
7.HI
-------
HYLEBOS WATERWAY
to a lesser extent, through the main outfall. The daily loading of the
chlorinated organic contaminants of concern to Hylebos Waterway from Occidental
Chemical Corporation is currently more than six times that of any other
source along the waterway.
Pennwalt Corporation appears to be a current source of chlorinated
ethenes, arsenic, copper, lead, zinc, and mercury. The chlorinated ethenes
are presently discharged to the waterway through the main plant outfall
and through groundwater which has become contaminated as a result of past
on-site waste disposal. Arsenic presently enters the waterway via the
main outfall and through groundwater that has become contaminated as a
result of on-site disposal of a sodium arsenite pesticide. The main plant
outfall appears to be a source of copper, lead, zinc, and mercury based
on effluent analyses and loading estimates. However, it is unclear why
process effluents at Pennwalt contain elevated concentrations of these
metals.
Kaiser Aluminum and Chemical Corporation has historically been a major
source of HPAH to Hylebos Waterway, principally via discharge through Kaiser
Ditch. Discharge of PAH through this ditch was much greater in the past
than it is at present, but there is evidence that some release of PAH
continues. Kaiser Ditch is also a source of arsenic, copper, lead, zinc,
and mercury. The relative contributions of Kaiser Aluminum and Chemical
and other properties bordering the ditch are unknown.
Hylebos Creek is an ongoing source of arsenic, copper, lead, and zinc.
The U.S. Gypsum landfill and the B&L Landfill are major contributors to
the arsenic load in Hylebos Creek. The arsenic contribution from the U.S.
Gypsum landfill should decrease with time as a result of recent remedial
action. Fife Ditch 1s the major contributor of zinc to Hylebos Creek.
Unpaved or partially paved log sorting yards bordering Hylebos Waterway
are sources of arsenic, copper, lead, and zinc because of the use of ASARCD
slag as ballast. As a group, these log sorting yards contribute approximately
11 lb/day of arsenic and 11 lb/day of metals (copper, lead, and zinc) via
surface runoff (contribution of Dunlap Towing was not quantified nor included
in total loading). Additional loading from the log sorting yards via
groundwater could be significant but is unquantified.
7.2.12.2 Recommendat ions--
Specific recommendations have been summarized at the end of each
contaminant section 1n Section 7.2. General recommendations for Hylebos
Waterway are listed below.
• Information on vertical and horizontal gradients of contamination
presented in this report should be used 1n evaluating future
requests for dredging permits and 1n determining the appropriate
chemical analyses prior to dredging. For example, prior
to Pennwalt's 1982 dredging, the firm analyzed surface sediments
in the area to be dredged for organic contaminants, and
7.112
-------
HYLEBOS WATERWAY
subsurface sediments for metals (High 1982). Based on the
data presented herein, peak concentrations of organic
contaminants are typically found in subsurface sediments,
while those of metals are generally found in surface sediments.
As a consequence of the dredging by Pennwalt, contaminated
sediments have been uncovered. In these newly exposed sediments,
concentrations of PCBs, chlorinated hydrocarbons, PAH, and
dibenzofuran were several times greater than those in nearby
surface sediment.
• The depth of sediment contamination often exceeded the effective
depth of penetration of the gravity and box core samplers
used in these investigations. Deeper samples probably requiring
a drilling program will be needed to assess adequately the
vertical extent of contamination prior to sediment removal
efforts.
7.113
-------
THIS PAGE LEFT INTENTIONALLY BLANK
7.114
-------
SITCUM WATERWAY
7.3 SITCUM WATERWAY
7.3.1 Introduction
It is uncertain when Sitcum Waterway was first created from the tidal
flats of the Puyallup River, but the waterway was filled with log rafts
in a 1923 photo of Commencement Bay. In this photo, the waterway was
approximately twice its present width. Little change appears in photographs
and charts of the waterway between 1923 and 1946. Since that time, nine
dredging operations have removed about 3.5 x 106 yd3 of waterway sediment
(Table 7.3.1). A portion of the dredged material was used as fill to form
new terminals along the north shore, reducing the width of the waterway
to its present size. This filled area comprises Terminal 7 and was completed
in 1973. The south shore of the waterway was dredged to form the West
Sitcum terminal in 1979. The channel has been dredged twice since 1979
for maintenance at Berth B, Terminal 7 and along the south shore of the
waterway mouth (Norton and Johnson 1985b; Port of Tacoma dredging Permits
6022, 6837).
Industries that used to occupy Sitcum Waterway waterfront include
lumber and wood products companies, railroad yards, and Time Oil Company,
an oil storage facility in the area from the 1930s to 1950s (Ruckelshaus
1985). Current industries along the waterway are shown in Figure 7.3.1.
The south shore is owned by the Port of Tacoma and leased by Sealand for
storage, shipping, and receiving facilities. An office building at the
head of the waterway houses the Port of Tacoma executive offices, formerly
(until 1982) located at the end of the south Sitcum peninsula (Dames and
Moore 1982). The north waterfront is occupied by the Port's Terminal 7,
with facilities for container handling and bulk unloading of alumina, various
ores, and concentrates. Two alumina storage domes at the terminal, built
in 1966 and 1968, have a combined capacity of 136,000 mt (Norton and Johnson
1985b).
Discharges to Sitcum Waterway, shown in Figure 7.3.1, include seventeen
storm drains and numerous discharges of unknown origin (presumably runoff).
The storm drain with the greatest discharge volume is SI-172, which serves
a large industrialized area between East 11th Street and Lincoln Avenue.
Two NPDES permitted industries (Georgia Pacific Corporation and Purex Corpora-
tion) discharge cooling water to Sitcum Waterway through this drain. Bnergency
overflow from a sewer 11ft station discharges to Sitcum Waterway via SI-176.
The bottom sediments of Sitcum Waterway have been heavily sampled,
particularly for the trace metals. Locations of surflclal sediment chemistry
sampling stations are shown 1n Figure 7.3.2, including both Tetra Tech
stations sampled as part of the Superfund investigations and all available
historical data. Although the Tetra Tech sampling was confined principally
to the central waterway, a great deal of historical data were available
to check for cross-waterway gradients of contamination.
7.115
-------
Table 7.3.1
DREDGING HISTORY OF SITCUM WATERWAY
Completed
1946
Contract
Number
19
1956
October
1961
February
1966
June
1968
1973
March
1979
September
1982
February
1983
49
99
179
214
339
456
488
525
Purpose and Amount
Initial dredging
2,736,800 yd3
385,000 yd*
Dredging for Terminal 7
Berths A 1 6
43,000 yd3
Dredging for Terminal 7
Berth C
Disposal
77,947 yd3
Dredging for Terminal 7
Berth D
Made West Sitcum terminal
Seal and (formerly TOTE
facility), 82,000 yd3
Maintenance dredging
Terminal 7, Berth B
29,708 yd3
West shoal dredging
90,000 yd3
Landfill bordered by east
11th Street, Lincoln Avenue,
Milwaukee Way, and Port of
Tacoma Road ("quadrangle")
Landfill adjacent to Sitcum
Waterway behind Terminal 7,
Berth A
Commencement Bay deepwater
disposal site
(no Information)
Commencement Bay deepwater
disposal site
(no information)
Landfill west side of Sitcum
Waterway.Sealand (formerly
TOTE facility)
Four Mile Rock, Elliott Bay
Commencement Bay deepwater
disposal site
Source: Norton and Johnson (1985); original Information from Gary Kucinskl, Port of
Tacoma
7.116
-------
Port of T«c««
tgt—,-wr»
v"*1 *££.1 *«»*»»
IW ***r~- M«U<
*"* a« i v-
•jXl'ilU.' c-»t«e«-
WSj^M
*"•" rt2
•nrf «•¦
vzst&sr 0
Sttcu* Waterway
Port of Tko®*
(Tote» Oc«w
E*p»*ss- 'nc
»*«*
t«C
¦y<*t
H»Cf «****

9t\f* \ Mflitl
Fit
•HW
l*f
arUMf**-*
i^siVV-02
""*0" Pactfic Ra
-------
v~ SI—165
SI-166
° Tio
tr. cr> <-*
o\
vo
SI-717

SI-172
A-4 A A 4
+ S-1
SI-716-01
1-9
S-2 +
ASI
SI-11DX
A7
S-15D SI-04 X
~ SI-13
SI-15
S-3 +
S-4
5A
I-IOZ SI-716-02
o
GO
SI—175
CO
~ Tetra Tech
A EPA
X Other Agencies
+ M00E, 1984
CO
Figure 7.3.2
SURFICIAL SEDIMENT STATIONS AND THE
SEDIMENT CORE LOCATION FROM ALL STUDIES
IN SITCUM WATERWAY
600
300
FEET
METERS
150
300
-------
SITCUM WATERWAY
The following were defined as preliminary contaminants of concern
in Siteurn Waterway:
Organic Compounds Inorganic Substances
Aromatic hydrocarbons Arsenic
Dibenzofuran Copper
Lead
Zinc
A discussion of spatial gradients, known discharges, and other potential
sources of these contaminants can be found in Sections 7.3.2 (aromatic
hydrocarbons and dibenzofuran) and 7.3.3 (metals).
Concentrations of each of these substances were later determined to
exceed toxicity or benthic AET in sediments from at least one station in
Sitcum Waterway. Additional substances present above AET (see Table 6.14
in Section 6) but not yet evaluated for sources include
Substance Station Where AET Exceeded
N-nitrosodiphenylamine SI-12
1-Methyl -(2-methyl ethyl benzene) S1-11
Diterpenoid hydrocarbons SI-12
The latter two compounds or compound groups are only tentatively identified.
These additional potential problem chemicals are not discussed further.
Average mass flux estimates were calculated for arsenic, copper, lead,
and zinc to enable a comparison of mass loadings of these contaminants
relative to their sediment concentrations. Insufficient source data were
available to calculate mass flux estimates for the other priority contaminants.
The mass flux estimates were evaluated using average concentrations of
the metals in sediments from all present and historical stations according
to the procedures and criteria outlined in Section 2.12.3.2. All of the
source-derived mass fluxes were within an order of magnitude of the concentra-
tion-derived mass fluxes. Therefore, according to the uncertainty criteria
for this analysis, no data gaps were indicated in accounting for major
sources of arsenic, copper, lead, or zinc.
7.3.2 Aromatic Hydrocarbons and Dibenzofuran
7.3.2.1 Spatial Distribution--
Low and high molecular weight polycyclic aromatic hydrocarbons (LPAH
and HPAH) and dibenzofuran have been identified as contaminants of concern
in Sitcum Waterway. The spatial pattern of contamination in surficial
sediments of the waterway was generally similar for all three contaminants
or contaminant groups (Figures 7.3.3-7.3.5). Based on data (dry-weight
basis) from the Tetra Tech stations in the center of the waterway, there
was evidence of a decreasing gradient from the head to the mouth of the
7.119
-------
- SI—165
(A)
mg/kg dry weight
si-166^
n P rs
S
/
0.34A AL1.8
I
£ ~
^ I
*/> m
tA
1
1.8°
*0.86
,1.2
¦U.S. EPA
STATION 3
"iga
z2.3dx
L1-5A n n Lh6n'^
I
~ 1 SI-172
*L2.5
dz1.7
SI-716-01
SI-716-02
\
SI—175
X.
* Exceeds AET (see Table 4.2 for AET values)
X
-SI—165
IB)
mg/kg TOC
SI-166
Zlioox
ozuo
SI-716-02
SI—175
METERS
SI-172
SI-716-01
~ Tetra Tech
A EPA
X Other Agencies
No organic carbon normalized AET exceeded
(see Table 4.6 for AET values)
Figure 7.3.3
CONCENTRATIONS OF LOW MOLECULAR WEIGHT PAH IN
SURFICIAL SEDIMENTS OF SITCUM WATERWAY
L = At least one of the components of the group was undetected,
sum included the detection limit.
Z = Data corrected for blank.
7.120
-------
- SI-165
SI*166
(A)
mg/kg dry weight
I
e -
I N
«/>
I
0.8A *L6
«/>
I
*L37
I
~ | ^SI-172
L5-6Ata(- SI-716-01
4.8*
L6.9a K
l2-4A n n n L3.9/1 sioit-02
\
SI-175
~24.9
X.
~ Exceeds AET (see Table 4.2 for AET values)
X
¦SI-165
SI-166
DZ120
(B)
rag/kg TOC
S
%
sn
12 ~
t>*4 K
I N
55 i
^ I j SI-172
Sl-716-01
~210
180A
2370
200
O Tetra Tech
A EPA
X Other Agencies
~ Z310
51-716-02
SI-175
METERS
No organic carbon normalized AET exceeded
(see Table 4.6 for AET values)
Figure 7.3.4
CONCENTRATIONS OF HIGH MOLECULAR WEIGHT PAH IN
SURFICIAL SEDIMENTS OF SITCUM WATERWAY
z « data corrected fotr blank
L ¦ At least one of the components
of the group was undected, sum
included the detection limit.
7.121
-------
•—SI-165
SI-166
(A)
mg/kg dry weight

o
1
Ot
o
I
o>

i
i
to
IH
U)

10
IN
I
ft*
r*»
r-4
R «
H K
I
»-• I
t/) W
V)
I
» I ^SI-172
~ 0.13
D0.11
DO.19
o n
SI-716-01
X
SI-716-02
\
SI-175

*¦ Exceeds AET (see Table 4.2 for AET values)
\
i— SI-165
SI-166
S
I
•»«
*>
I
vd
i
to
I
(B)
mg/kg TOC
* r
r«»
H I H
K *-4 I
i ** 5*
i '1 /"""
~ 5.3
~ 6.1
~ 12
~15
L38*
ilji n
SI-716-01
N
SI-716-02
\
SI-175
300 600
I FEET
~ Tetra Tech
# Exceeds AH (see Table 4.6 for AET values)
METERS
Figure 7.3.5
CONCENTRATIONS OF DIBENZOFURAN IN
SURFICIAL SEDIMENTS OF SITCUM WATERWAY
7.122
-------
SITCUM WATERWAY
waterway. However, when all available data were considered, no definitive
gradient was apparent and the distribution was patchy. TOC data were available
for only some of the stations in the combined data sets. However, there
was no gradient observed after concentrations were normalized to organic
carbon content (Figures 7.3.3-7.3.5).
An isolated area with elevated concentrations (dry weight) was apparent
for LPAH, HPAH, and dibenzofuran near the waterway mouth along the southern
shore (Tetra Tech SI-14 and U.S. EPA Station 3; see locations in Figure
7.3.2). These stations are located near the Sealand facility in an area
recently disturbed by dredging. Therefore, it is likely that the observed
elevated concentrations were from historical deposition.
One sediment core sample was collected at the head of Sitcum Waterway
along the Terminal 7 pier face, near the northeast corner. Concentrations
(ug/kg dry weight) with depth in the sediment were
LPAH HPAH Dibenzofuran
Horizon 1 (0-0.10 m) 2,040 8,100 235
Horizon 2 (0.10-0.30 m) 6,900 25,300 430
Horizon 3 (0.30-0.41 m) 1,740 4,500 170
These data indicate a subsurface maximum in PAH and dibenzofuran concentra-
tions. Concentrations in Horizon 2 were two-fold to five-fold greater
than those in shallower or deeper horizons and exceeded toxicity and benthic
AET. Concentrations 1n Horizons 1 and 3 did not exceed AET.
7.3.2.2 Loading Estimates--
The effluent from drains SI-172 and SI-175 have been analyzed for
LPAH and HPAH. In two analyses with detection limits of 10 ug/L, no LPAH
or HPAH were measured in the effluent from drain SI-175. Only a single
LPAH, phenanthrene, was detected in six analyses of the effluent from drain
SI-172. On one occasion, the phenanthrene concentration was reported to
be less than 0.30 ug/L (W00E unpublished). Only a single HPAH, pyrene,
has been detected in discharge from drain SI-172. In one of six analyses,
the pyrene concentration was less than 0.20 ug/L (WD0E unpublished). No
HPAH were reported 1n five other analyses with detection limits ranging
from 0.1 to 10 ug/L. Dibenzofuran was undetected at 0.1 ug/L in two analyses
of the SI-172 effluent.
7.3.2.3 Source Identif1cat1on--
No apparent sources of PAH and dibenzofuran can be Identified. Storm
drains and runoff Into the waterway are a potential source. There is no
documented source to account for the area near the south shore at the mouth
of the waterway where LPAH and dibenzofuran concentrations exceed those
elsewhere 1n the waterway. Tacoma Boatbuilding Company was located on
the waterfront 1n this area until the 1970s. "Hie company relocated to
Hylebos Waterway after their operation was destroyed by fire, and the site
7.123
-------
SITCUM WATERWAY
was occupied by Aero Jet, a hovercraft manufacturer. After the departure
of Aero Jet (late 1975), the Port of Tacoma moved their offices to this
site. In 1982, the Port moved their offices to the head of the waterway,
and the site at the mouth was subsequently leased to Totem Ocean Trailer
Express, then to Sealand, the present leasee. It is possible that activities
of one or more of the previous occupants contributed to the PAH in the
waterway sediments. The fire at Tacoma Boatbuilding would also have contributed
an unquantifiable amount of PAH to the waterway sediments. However, another
likely cause of the elevated contaminants in this area is exposure of buried
contaminated sediments during the dredging of several feet of sediments
by the Port of Tacoma in the early 1980s.
Milwaukee Railroad was located on the south shore of Sitcum Waterway
until 1980. According to Dames and Moore (1982), numerous solid and liquid
spills have occurred in this area. The contents of these spills are unknown
and the associated potential for release of contaminants to Sitcum Waterway
from the spills and railway operations cannot be evaluated. Time Oil Company
(gasoline and oil storage) was located somewhere in Sitcum Waterway area
from the 1930s to 1950s. No other information is available on this company.
Based on a review of WDOE Environmental Complaint Files, 1978-1985,
two recent spills could have contributed contaminants to the waterway.
On March 25, 1981, 150 gal of Bunker C oil was spilled at the intersection
of East 11th Street and Port of Tacoma Road. On November 12, 1983, less
than 500 gal of diesel and Bunker C oil were spilled in Sitcum Waterway
(point of discharge not established).
7.3.2.4 Summary and Recommendations--
No major sources of PAH and dibenzofuran could be identified. General
discharges by storm drains and runoff 1s the major suspected source. The
isolated area near the mouth of the waterway where highest LPAH and dibenzo-
furan concentrations were measured is most likely attributable to a dredging
project that may have exposed deeper, more contaminated sediments. The
composition of PAH (i.e., an abnormally high benzo(a)pyrene concentration)
at this station was unlike that of other station in the waterway.
General controls on petroleum products and suspended matter in storm
drain systems should be considered.
7.3.3 Metals
7.3.3.1 Spatial Distrlbution--
The spatial distributions of copper, zinc, and lead 1n surficial sediments
of Sitcum Waterway are shown 1n Figures 7.3.6-7.3.8. Data from Tetra Tech
stations suggested a possible trend 1n the central waterway with concentra-
tions decreasing towards the mouth. This trend disappeared when all available
data were considered. Instead, the distribution was patchy, with concentration
elevations along the north shore and a definite hot spot 1n the northeast
corner (U.S. EPA station). The distribution of arsenic was patchy with
7.124
-------
SI-165
SI-166
METERS
(A)
mg/kg dry weight
H
o
CM
O
t
r«*
at
at
rH
i
r**
i
r»*
i
*—•
v»
to
tn

S
/
140 A ^210
74° *1600*
*2100£
+ 290
~ 160
+350*
*680a
1
*340A
~ Tetra Tech
A EPA
X Other Agencies
+ WDOE, 1984
*580 A
290 ~
230+ AVe
fUl n 3io
* Exceeds AET (see Table 4.1 for AET values)
SI-172
SI-716-01
S J-716-02
SI-175
Figure 7.3.6
CONCENTRATIONS OF COPPER IN
SURFICIAL SEDIMENTS OF SITCUM WATERWAY
7.125
-------
-SI—165
SI-166
METERS
(A)
mg/kg dry weight
~ Tetrs "lech
A EPA
X Other Agencies
+ WDOE, 1984
s
/

*300 ^ *700*
~100 *1700*
o£130
I
«/)
1
1
* \ ^ SI—172
+980* *1300 A *910+*HOOA
noEn *1200a
rA* 0340 *490DX1100*
t v
SI-175
tL I
uoo*
*lv
a »-
-716-01
716-02
\
* Exceeds AET (see Table 4.1 for AET values)
\
Figure 7.3.7
CONCENTRATIONS OF ZINC IN
SURFICIAL SEDIMENTS OF SITCUM WATERWAY
7.126
-------
- SI-165
SI-166
METERS
(A)
mg/kg dry weight
. CM
O ? ^
0> M
R ^
K
I
M I
(A «
«/>
250a *620*
*790*
8*
I
~ ( j SI-172
+ 1240*^Q2oa *i900+*450Aig5(|tsi
D500* *660° *420*
1a,ha n *480+*W k
*430A J1 n fl *490JNl-
-716-01
~ Tetra Tech
A EPA
X Other Agencies
+ WDOE. 1984
716-02
\
SI-175
\
* Exceeds AET (see Table 4.8 for AET values)
\
Figure 7.3.8
CONCENTRATIONS OF LEAD IN
SURFICIAL SEDIMENTS OF SITCUM WATERWAY
7.127
-------
SITCUM WATERWAY
no apparent gradients or hot spots (Figure 7.3.9). Normalization of metals
concentrations to percent fine-grained material in Sitcum Waterway sediments
did not substantially change the relative distribution observed. Grain
size data were not available for several stations with the highest metals
concentrations.
One sediment core sample was collected at the head of Sitcum Waterway
along the Tenminal 7 pier on the north shore. The data (Table 7.3.2) indicate
a subsurface maximum for all the metals of concern. The second horizon
(0.1-0.3 m) had greater concentrations of copper, lead, zinc, and arsenic
than did horizons above and below.
7.3.3.2 Loading Estimates--
There are seven discharges to Sitcum Waterway for which calculated
loadings of arsenic, copper, lead, and zinc were available. Loadings from
the seven storm drains, along with data on concentrations and flow from
each source, are summarized in Tables 7.3.3-7.3.6. These determinations
were made using all available loading data. Drain SI-172, a 60-in concrete
pipe storm drainage outfall entering the northeast corner of the waterway,
discharged 93 percent of the total arsenic loading to Sitcum Waterway.
The same drain was also the primary source of copper. Other major sources
of copper loading were drain SI-176 (a 30-in concrete pipe outfall entering
1,200 ft from the head of the waterway on the south shore) and drain SI-717
(under Pier 7). Drain SI-716 was the primary source of both lead and zinc.
Drains SI-172 and SI-717 were also important sources of lead and zinc.
An investigation by Norton and Johnson (1985) during a storm event
in 1984 indicated that drain SI-172 accounted for 80 to 90 percent of the
total zinc, copper, and lead loading and 98 percent of the arsenic loading
to the waterway. Ten drains were sampled during the investigation. Loading
estimates by Tetra Tech and Norton and Johnson (1985) differ because Tetra
Tech's loading calculations are based on all available data, while Norton
and Johnson's loading calculations are based on a single event.
7.3.3.3 Source Identification--
Observed spatial distributions, along with the loading data presented
above, implicate four sources as the major contributors of metals to Sitcum
Waterway: 1) the Port of Tacoma ore docks, 2) drain SI-172 discharging
to the northeast corner of the waterway, 3) drain SI-176 discharging midway
along the south shore of the waterway, and 4) drain SI-717 discharging
to the head of the waterway along the north shore. Each potential source
is discussed Individually below.
Port of Tacoma Ore Docks--Elevated concentrations of copper, lead,
and zinc along the north shore :annot be accounted for by discharge from
any storm drain system. Substantially higher concentrations of these contam-
inants were found in surficial sediments 1n the vicinity of Terminal 7
along the north shore of the waterway than 1n those along the south shore.
7.128
-------
SI-165
S -166
METERS
(A)
mg/kg dry weight
S
/
57^ 65
~10 *470*
23^ n
+ 66
°28
+210*
A170*
fN.
I
«/>
R «4
S i
(/>
iSO
l i J St—172
*180&
~ Tetra Tech
A EPA
X Other Agencies
+ WDOE, 1984
+1102DM?
*290*..
53 +
93 ~?
A 440
*160*
u rUSi
SI-716-01
SI-716-02
\
SI-175
\
* Exceeds AET (see Table 4.1 for AET values)
\
Figure 7.3.9
CONCENTRATIONS OF ARSENIC IN
SURFICIAL SEDIMENTS OF SITCUM WATERWAY
7.129
-------
Table 7.3.2
CONCENTRATIONS OF ARSENIC AND METALS
WITH DEPTH IN THE SEDIMENT
STATION SI-60, B02
Contaminant
Copper Lead Zinc Arsenic
Hori zon
1
(0-0.10 m)
471
1,240
939
150
Horizon
2
(0.10-0.30 m)
669
1,670
1,100
210
Horizon
3
(0.30-0.41 m)
128
160
50
44
Concentrations in mg/kg dry weight
7.130
-------
Table 7.3.3
ARSENIC: SUMMARY OF LOADINGS FROM DISCHARGES TO THE SITCUM WATERWAY

Drain f
Drain Name
Flow (HGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)
SI-172
Storm Drain System
0.81
(0.11-5.2)
(n-9)
3/29/82-6/29/84
264
(4.5-1,750)
(n-10)
1.8
(.03-11.82)
SI—175
24-Inch Concrete Pipe
0.088
(.09-.086)
(n-2)
6/26/84
5.5
(1-10)
(n-2)
0.0040
(.00073-.0073)
SI-176
30-1nch Concrete Pipe
0.39
(n-1)
6/26/84
21
(n-1)
0.068
SP-716
PVC Pipe
0.044
(n-1)
6/26/84
9.5
(n-1)
0.0035
51-717
Drain under Pier 7
0.56
(n-1)
6/26/84
12
(n-1)
0.056
SI-718
Bulkhead Drain
0.013
(n-1)
6/26/84
9
(n-1)
0.0098
SI-719
Concrete Drain Pipe
.053
(n»l)
6/26/84
5.5
(n-1)
0.0024
7.131
-------
Table 7.3.4
COPPER: SUMMARY OF LOADINGS FROM DISCHARGES TO THE SITCUM WATERWAY

Drain I
Drain Name
Flow (HGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(f of Observations)
Loading (lbs/day)
(Avg. and Range)

SJ-172
Storm Drain System
0.81
(0.11-5.2)
(n-9)
3/29/82-6/29/84
84.5
(30-176)
(n-6)
0.57
(.20-1.19)
SJ-175
24-Inch Concrete Pipe
0.088
(.09-.086)
(n-2)
6/26/84
41
(n-1)
.030
SI-176
30-Inch Concrete Pipe
0.39
(n-i)
6/26/84
118
(n-1)
0.38
SP-716
PVC Pipe
0.044
(n-1)
6/26/84
48
(n-1)
0.018
SI-717
Drain under Pier 7
O.S6
(n-1)
6/26/84
78
(n-1)
0.36
SI-718
Bulkhead Drain
0.013
(£i)
6/26/84
64
(n-1)
0.0069
SI-719
Concrete Drain Pipe
.053
(n-1)
6/26/84
61
(n-1)
0.027
7.132
-------
Table 7.3.5
LEAD: SUMMARY OF LOADINGS FROM DISCHARGES TO THE SITCUM WATERWAY

Drain #
Drain Name
Flow (MGD)
(Avg. and Range)
(I of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)

SI-172
Storm Drain System
0.81
(0.11-5.2)
(n-9)
3/29/82-6/29/84
53.3
(12-199)
(n-10)
0.36
(0.081-1.34)
SI—175
24-1nch Concrete Pipe
0.088
(.09-.086)
(n-2)
6/26/84
30
(20-40)
(n-2)
0.022
(0.015-0.029)
SI—176
30-Inch Concrete Pipe
0.39
(n-i)
6/26/84
479
(n-1)
1.56
SP-716
PVC Pipe
0.044
(n-1)
6/26/84
76
(n-1)
0.028
Sl-717
Drain under Pier 7
0.56
(n-1)
6/26/84
193.5
(n-1)
0.90
SI—718
Bulkhead Drain
0.013
(n-1)
6/26/84
53
(n-1)
0.0057
SI-719
Concrete Drain Pipe
.053
(n-i)
6/26/84
191
(n-1)
0.084
7.133
-------
Table 7.3.6
ZINC: SUMMARY OF LOADINGS FROM DISCHARGES TO THE SITCUM WATERWAY
Drain #
Drain Name
Flow (HGD)
(Avg. and Range)
(I of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)

SI-172
Storm Drain System
\
0.81
(0.11-5.2)
(n-9)
3/29/82-6/29/84
181.9
(60-553)
(n»10)
1.2
(0.41-3.74)
SI-175
24-Inch Concrete Pipe
0.088
(.09-.086)
(n-2)
6/26/84
272.5
(155-390)
(n-2)
0.20
(0.11-0.29)
SI—176
30-Inch Concrete Pipe
0.39
(n-1)
6/26/84
537

0.030
SI-719
Concrete Drain Pipe
.053
(n-i)
6/26/84
244
(n-1)
0.11
7.134
-------
SITCUM WATERWAY
Terminal 7 has facilities for handling and bulk unloading of alumina, metal
ores, and ore concentrates. Copper, lead, and zinc ores handled at Terminal
7 are probable sources of these contaminants in Sitcum Waterway. As noted
by Norton and Johnson (1985), spillage occurs in the dock area in the process
of unloading ore. It is the practice of the Port of Tacoma to sweep up
material that can be recovered and to wash the remainder into the waterway.
Drain SI-172--From the available information, SI-172, the North Corner
drain, appears to be a major source of metals to Sitcum Waterway. Two
facts point to this conclusion. First, the highest concentrations of arsenic
(288 mg/kg), copper (7,000 mg/kg), and zinc (3,200 mg/kg), and the second
highest concentration of lead (1,900 mg/kg) in surficial sediments of the
waterway were found intertidally at the outfall of the North Corner drain.
Second, the North Corner drain contributed 93 percent of the quantified
arsenic loading to the waterway, 41 percent of the copper, 12 percent of
the lead, and 27 percent of the zinc. [These percentages are not consistent
with those provided by Norton and Johnson (1985). Norton and Johnson used
data from a single storm event in June, 1984, whereas the loadings shown
herein are based on an average of 6 to 10 analyses of SI-172 effluent over
several years.]
The watershed of the tideflats from which runoff would be discharged
to Sitcum Waterway through SI-172 is shown in Figure 7.3.1. The area is
bounded by East 11th Street, Lincoln Avenue, Port of Tacoma Road, and Milwaukee
Way. This area is occupied by a number of small to moderate-sized industries,
many of which could be contributors of the metals loading from SI-172.
It is impossible to determine the ultimate sources of metals from this
discharge with the available data.
Allied Chemical is the only industry within the SI-172 drainage area
at which operations have resulted in known environmental contamination
by trace metals. The firm produces aluminum sulfate and has historically
disposed of wastes in on-site ponds. As a result of this practice, groundwater
has become contaminated with sulfate (up to 14,000 mg/L), chromium (up
to 0.55 mg/L), zinc (up to 2.3 mg/L), and aluminum (up to 2,300 mg/L) (Hart-
Crowser and Associates 1983a,b). A slight elevation 1n lead concentrations
beneath the waste ponds was Indicated, although it is not among the primary
waste constituents. No data are available for copper.
A recent groundwater study of the Allied Chemical site (Hart-Crowser
and Associates 1983b) found that within an exploration depth of 10 m, both
an upper and middle sand aquifer have become contaminated. Contaminants
were reported to be migrating west and south of the site 1n the upper aquifer
and north-northeast in the middle aquifer. This Indicates that contamination
1n the upper aquifer may Impact water and sediment quality 1n Sitcum Waterway,
although there are Insufficient data to adequately characterize off-site
groundwater flow and determine the actual area of discharge. Hart-Crowser
and Associates (1983b) suggested that, with the possible exception of zinc
and aluninun, any other metals associated with the wastes would be immobilized
by adsorption to soil particles and would not migrate far off-site.
7.135
-------
SITCUM WATERWAY
Drain SI-176--This drain discharges surface water runoff midway along
the south shore of Sitcum Waterway. This storm drain serves the 170-ac
Sealand facility located on the south side of the waterway. Based on a
single analysis, it contributes 53 percent of the quantified lead loading,
38 percent of the zinc, and 27 percent of the copper to Sitcum Waterway.
The source of metals within the drainage area of SI-176 is unknown.
Metal ores have not been unloaded on this side of the waterway (Kucinski,
G., 9 August 1985, personal communication). A potential source may be
the leaching of metals from ASARCO slag that was used to riprap the southern
shore. Source investigation may be necessary to determine the source of
metals in discharge SI-176. Additional sampling also may be justified
to confirm the significance of this source, since loading estimates were
based on a single sampling event.
Drain SI-717--This drain discharges surface water runoff near the
head of the waterway along the north shore. Based on a single analysis,
it contributes 35 percent of the quantified copper loading, 30 percent
of the lead, 27 percent of the zinc, and 3 percent of the arsenic to Sitcum
Waterway. The origin of this discharge was not established during these
investigations, although judging from its location, it may carry runoff
from the Port's ore handling facilities on Terminal 7. Further efforts
may be warranted to determine the source of the discharge and to better
quantify its metals contribution.
Cascade Pole may also be a source of metals, although there was no
evidence in the available data of elevated sediment contaminant concentr-
ations attributable to this site. From 1936 to 1975, Cascade Pole was
located near the head of the waterway on the north shore. This firm treated
wood with pentachlorophenol, creosote, chrome, and arsenic and may have
been a historical source of arsenic (in addition to other contaminants
not identified to be of concern in Sitcum Waterway). There was no evidence
of elevated arsenic concentrations in the area of the waterway nearest
Cascade Pole that cannot be explained by arsenic input from the SI-172
storm drain.
7.3.3.4 Summary and Recommendations-
Four ongoing sources of copper, lead, zinc, and arsenic have been
identified:
• The elevated metal concentrations along the north shore
are believed to be a result of ore spillage from the Port
of Tacoma ore docks. Copper, lead, and zinc ores are off-
loaded at the facility and spillage 1s typically washed
into the waterway.
• The North Corner storm drain (SI-172) 1s the major source
of arsenic to Sitcum Waterway, contributing 93 percent of
the total quantified loading. It is also a significant
source of copper, lead, and zinc.
7.136
-------
SITCUM WATERWAY
• Drain SI-176, which discharges along the south shore, is
a source of copper, lead, and zinc. The source of metals
to this drain has not been determined.
• Drain SI-717, which discharges along the north shore near
the head of the waterway, is a source of copper, lead, and
zinc. The source of metals to this drain has not been determined
but may be associated with the Port's ore handling facili-
ties.
Loadings of metals to Sitcum Waterway could be dramatically reduced
if source control efforts were initiated to minimize or eliminate discharges
from the ore docks and drains SI-172, SI-176, and SI-717. However, the
metals already in the waterway sediments would be expected to remain there,
except as moved or buried by sediment transport and deposition. There
are no reliable estimates available by which to predict the rate of these
processes.
Three recommendations can be made based on the results of the source
identification efforts:
• Spillage of ore from the Port of Tacoma facilities on the
north shore should be minimized or eliminated. Alternatives
to washing spilled ore into the waterway should be investigated.
• Drain SI-172 serves a large area occupied by numerous small
to moderate-sized industries. Since this drain contributes
the vast majority of arsenic to the waterway, as well as sig-
nificant quantities of other metals, the ultimate sources
of metals within the drainage basin should be Identified.
The transportation route of the ore material should be investi-
gated. Even if the sources cannot be identified, construction
of settling basins or similar facilities could be used to
reduce the particulate load and, therefore, the metals load
of this discharge.
• The importance of drains SI-717 and SI-176 as sources of
metals should be verified by additional sampling since the
conclusions presented herein are based on a single analysis.
If the drain is shown to be a major contributor of metals,
then the source of these metals to the drain should be
identified.
7.137
-------
ST. PAUL WATERWAY
7.4 ST. PAUL WATERWAY
7.4.1 Introduction
St. Paul Waterway was created in stages from 1920 to the early 1930s
(Dames and Moore 1982). Its basic outline extended to 11th Street in a
1923 chart of the tideflats area (Hart-Crowser and Associates undated).
A 1946 chart indicates that the inner portion of the waterway was used
for log rafts and booms and was navigable to shallow draft boats (Hart-Crowser
and Associates undated). It is likely that this part of the waterway remained
tidal and was never dredged (Stargell, W., personal communication). In
the early 1960s, the head of the waterway was filled to create the current
configuration, which is about half its former size. Fill material is believed
to have come from the Army Corps of Engineers dredging of the Puyallup
River (Stargell, W., personal communication) and may have included slash
and sawdust from Champion International (Dames and Moore 1982).
Champion International (formerly St. Regis Paper Company) occupies
the land surrounding St. Paul Waterway (Figure 7.4.1), including the area
at the head of the waterway filled in the 1960s. Current operations consist
of a stud mill, pulp and paper mill, bag manufacturing plant, distribution
yard, log storage yards, and an industrial supply section(Stargel1, W.,
personal communication). In the past, operations included a veneer plant
and a factory constructing panelized structures and modular homes (Ruckelshaus
unpublished). Paxport Mills manufactures cedar fencing and alder paneling
at their sawmill on the waterway's west peninsula. The mill has operated
since the late 1960s.
Land use surrounding St. Paul Waterway has been restricted to the
forest products industry. The St. Paul and Tacoma Lumber Company was the
first industry located near the St. Paul Waterway and the first constructed
in the tideflats area. The mill opened in 1889 on "The Boot," a tideflat
area now bounded by Wheeler-Osgood Waterway, the Puyallup River, East 11th
Street, and Puyallup Avenue (Morgan and Morgan 1984). The St. Regis paper
company expanded its operation on the St. Paul waterfront from its original
location along the Puyallup River when it bought land from the St. Paul
and Tacoma Lumber Company in 1940. In the 1930s and 1940s, Donald W. Lyle
operated a plywood cutting operation and log bay along St. Paul Waterway
(Ruckelshaus unpublished). In 1959, St. Regis (now Champion International]
acquired the St. Paul and Tacoma Lumber Company (Stargell, W., personal
communication). Champion International is currently the only industry
along St. Paul Waterway.
Discharges to St. Paul Waterway are shown 1n Figure 7.4.1. Champion
International has the only NPDES-permitted discharge (SP-189), located
at the end of the east peninsula separating the St. Paul Waterway and Rjyallup
River via PU-190. Champion continues to use this outfall periodically
during plant upsets or treatment malfunctions. This discharge has been
1n use since 1970. Earlier, Champion (then St. Regis) discharged to the
Puyallup River via PU-190. Champion continues to use this outfall periodically
as a bypass during plant upsets or treatment malfunctions. The current
7.138
-------
SP-189
Champion
International
NPDES WA0000850
PU-190

SP-706 SP-269

SP-268-01
SP-268-02

Figure 7.4.1

MAJOR INDUSTRIES AND DISCHARGES TO
THE ST. PAUL WATERWAY
\
*
\
» •
~ •
Champion
.rnational
Inte>
Qj
Qji
t. y
0/
to/.
U/
!$
-------
ST. PAUL WATERWAY
discharge has permit limits on BOD, pH, and suspended solids. Champion
International is also required to report discharge temperature and total
production. Two 24-in storm drains (SP-268-01 and SP-268-02) also discharge
to the south end of the waterway.
The location of sediment chemistry stations in St. Paul Waterway,
including those sampled as part of the Superfund investigation and all
historical sampling sites, are shown in Figure 7.4.2. Stations designated
to be of concern in these investigations are SP-13, SP-14, SP-15, and SP-16
located at the mouth of the St. Paul Waterway and in Commencement Bay north
of the waterway. Contaminants or contaminant groups designated to be of
preliminary concern at these stations include
Organic Compounds Inorganic Substances
Organic enrichment
Alkylated phenols Copper
Methoxyphenols
1-Methyl(2-methyl ethyl)benzene
Naphthalene
Methylnaphthalene
The spatial distributions, known loadings, and potential sources of these
compounds are discussed below. Chloroform was detected at elevated concen-
trations in a 1981 WDOE Class II survey of the Champion International effluent
and receiving waters (Yake 1982b). This volatile compound was undetected
in all sediment samples analyzed from St. Paul Waterway at a detection
limit of 10 ug/kg dry weight. Chloroform was also undetected (5 ug/kg
wet weight) in four English sole muscle tissue samples from St. Paul Waterway.
Therefore, chloroform is not a chemical of concern with respect to sediment
contamination or bioaccumulation.
Concentrations of the preliminary contaminants of concern listed above
were later determined to exceed toxicity or benthic AET in sediments from
at least one station in St. Paul Waterway. The one exception was copper,
which was of concern because of its significant bioaccumulation in English
sole muscle tissue. Copper concentrations did not exceed toxicity or benthic
AET in any surface or subsurface sediment sample from St. Paul Waterway.
Other substances that were present above AET at a single station only (Priority
3 chemicals; see Table 6.14 1n Section 6) but for which sources have not
yet been evaluated include:
Substance Station Where AET Exceeded
Phenol SP-14
Benzyl alcohol SP-13, SP-14, SP-16
Nickel SP-14
Additional tentatively Identified chemicals present above AET include
retene (Station SP-16 only), two diterpenoid hydrocarbons (Stations SP-14
7.140
-------
SP-16D
Sediment Core
A-2A
~ Tetri Tech
OHD0E. Historical
A EPA
X Other Agencies
SP-13Q
SP-706 SP-269
SUM18*
SP-268-01
SP-268-02
300 600
Figure 7.4.2
SURFICIAL SEDIMENT STATIONS AND SEDIMENT CORE LOCATIONS
FROM ALL STUDIES IN THE ST. PAUL WATERWAY
7.141
-------
ST. PAUL WATERWAY
and SP-15), and biphenyl (Station SP-14 only). Total volatile solids were
also above AET at Station SP-14 only. These substances are not discussed
further.
Average mass flux estimates were calculated only for copper and naphthalene
in St. Paul Waterway. Source data for other contaminants were insufficient
for analysis. Mass flux estimates for copper and naphthalene were evaluated
using average concentrations of these contaminants in sediments from all
present and historical stations according to the procedures and criteria
outlined in Section 2.12.3.2. When calculating the source-derived mass
flux, potential copper loadings from the Puyallup River (Table 7.4.3) were
excluded because of uncertainties concerning the appropriate dilution factor.
Even without this loading component, the source-derived mass flux for copper
still exceeds the sediment concentration-derived mass flux by an order
of magnitude. The corresponding source-derived mass flux for naphthalene
is less than the concentration-derived mass flux by an order of magnitude.
According to the uncertainty criteria for this analysis, no data gaps were
indicated in accounting for major sources of naphthalene or copper, even
when contributions from the Puyallup River are ignored.
7.4.2 Spatial Distribution
Spatial distributions of contaminants of concern in surficial sediments
of St. Paul Waterway are shown in Figures 7.4.3-7.4.9. All contaminants
showed similar concentration gradients, with the highest concentration
(dry-weight basis) at Station SP-14. Contaminant concentrations at this
station were 1.5 to 30 times greater on a dry-weight basis than those at
any other station in St. Paul Waterway. The proximity of discharge SP-189
to this area of elevated contaminant concentrations suggests that SP-189
is the major source of the contaminants.
Contaminated sediments at Station SP-14 off discharge SP-189 contained
high levels of TOC (16 percent). Similar levels of organic enrichment
were not found at any other station in St. Paul Waterway (Figure 7.4.3).
This TOC distribution Indicated dilution of sediments beyond the immediate
vicinity of Station SP-14 by relatively organic-poor material from other
sources (e.g., the Puyallup River). Although the lowest concentrations
of organic carbon in St. Paul Waterway were found at Stations SP-15 and
SP-16 (TOC +2 percent) adjacent to Station SP-14, these sediments remained
substantiaTly contaminated by organic compounds and metals on a dry-weight
basis.
After normalization to organic carbon among these stations, 4-methvlphenol
concentrations steadily decreased with distance from Station SP-14 (Figure
7.4.4). This spatial pattern strongly suggests a single source of 4-methyl-
phenol originating at discharge SP-189, the main outfall of Champion
international. Concentrations of other organic contaminants normalized
to TOC (Figures 7.4.5-7.4.8) did not show a similar gradient, but the highest
concentrations (TOC basis) of 2-methoxyphenol and 1-methyl (2-methyl ethyl) benzene
were still found in the area defined by Stations SP-14, SP-15, and SP-16.
7.142
-------
1.5 O
2.8 A
0 300 600
I FEET
~ Tetra Tech
A EPA
X Other Agencies
\
\
SP-706 SP-269
5.7 O
METERS
SP-268-01
SP-268-01
* Exceeds AET
(see Table 4.3 for AET values)
Figure 7.4.3
CONCENTRATIONS OF TOTAL ORGANIC CARBON (%)
IN THE SURFIC1AL SEDIMENTS OF THE
ST. PAUL WATERWAY
7.143
-------
*96000 D
*2600 ~
890 ~*
*1900 ~
'SP-189

yp .
e/.
PU-190
SP-706 SP-269
SP-268-01
SP-268-02
(A)
ug/kg dry weight
v
\
* Exceeds AET
(see Table 4.2 for
AET values)
*61 ~
o 300 eoo
I FEET
~ Tetra Ttch
SP-268-01
SP-268-02
* Exceeds AET
(see Table 4.6 for
AET values)
Figure 7.4.4
CONCENTRATIONS OF 4-METHYLPHEN0L
IN THE SURFICIAL SEDIMENTS OF THE
ST. PAUL WATERWAY
7.144
-------
(A)
yg/kg dry weight
340 ~
PU-190
*3900 D
*1500 °
560 ~
SP-706 SP-269
SP-268-01
SP-268-02
* Exceeds AET
(see Table 4.2 for
AET values)
23* ~
0 300 600
[feet
METERS
~ Tetra Tech
SP-268-01
SP-268-02
*Exceeds AET
(see Table 4.6 for
AET values)
Figure 7.4.5
CONCENTRATIONS OF 2-METHOXYPHENOL
IN THE SURFICIAL SEDIMENTS OF THE
ST. PAUL WATERWAY
7.145
-------
(A)
pg/kg dry weight
300 ~
PU-190
*6600 ~
*1400 ~
SP-706 SF-269
* Exceeds AET
(see Table 4.2 for AET values)
SP-268-01
SP-268-02
20 ~
0 300 600
I FEET
~ Tctra Tech
150 300
* Exceeds AET
(see Table 4.6 for AET values)
METERS
SP-268-01
SP-268-02
Figure 7.4.6
CONCENTRATIONS OF 1-methy1-2-(1-methylethyl)benzene
IN THE SURFICIAL SEDIMENTS OF THE
ST. PAUL WATERWAY
7.146
-------
(A)
ug/kg dry weight
*7200
*4400 ~
290 ~
\
Pu-190
270 ~
*2700 ~
SP-706 SP-269
1100
* Exceeds benthlc effects
and toxicity AET of
2100 ug/kg DW
1400 X
SP-268-01
SP-268-02
METERS
~ Tetra Tech
0 WOE, Historical
ACM
X Other Agencies
* Exceeds toxicity AET of 99 mg/kg'
TOC (benthlc effects AET
N170 mg/kg TOC but not
estabi'shed]
SP-268-01
SP-268-02
Figure 7.4.7
CONCENTRATIONS OF NAPHTHALENE
IN THE SURFICIAL SEDIMENTS OF THE
ST. PAUL WATERWAY
7.147
-------
110
\
SP-268-01
SP-268-02
~ Exceeds benthlc effects
and toxicity AET of
670 ug/kg DW
7.5 ~
0 300 600
I FEET
~ Tctrt Tacit
Toxicity AET of 38 mg/kg TOC
not exceeded (benthlc effects
AET >64 but not established)
•SP-268-01
SP-268-02
Figure 7.4.8
CONCENTRATIONS OF 2-METHYLNAPHTHALENE
IN THE SURFICIAL SEDIMENTS OF THE
ST. PAUL WATERWAY
7.148
-------
16<>
(A)
mg/kg dry weight
160
280 ~ i
32 ~
SP-1B9

29 ~
Ol80
r>V,

X
\
82 O
PU-190
SP-706 SP-269
A 100
SP-268-01
SP-268-02
No dry weight normalized AET exceeded
(B)
mg/kg fines
300 600
FEET
52.9
A 140
~ Tetra Tech
0 WD0£, Historical
A CPA
X Other Agencies
410D
120 ~
PU-190
SP-706
SP-269
- SP-268-01
** SP-268-02
'No fine grained material normalized AET exceeded
Figure 7.4.9
CONCENTRATIONS OF COPPER IN THE SURFICIAL SEDIMENTS
OF THE ST. PAUL WATERWAY
7.149
-------
ST. PAUL WATERWAY
Concentrations of naphthalene normalized to organic carbon were highest
in sediments from Station SP-12 near discharge SP-706 (Figure 7.4.7), while
normalized concentrations of 2-methylnapthalene (a related hydrocarbon)
were similar among all stations in St. Paul Waterway (Figure 7.4.8). This
pattern differed from that of 4-methylphenol normalized to organic carbon
and indicated that these hydrocarbons likely derive from different sources
in St. Paul Waterway. At least two sources of copper are also indicated
in St. Paul Waterway because high concentrations of copper (dry-weight
basis) were found at Station SP-14 and at a well-removed historical station
near the head of the waterway (Figure 7.4.9). Although grain size data
were not available for all historical stations, copper concentrations normalized
to percent fine-grained material also showed consistent evidence of at
least two sources of copper (Figure 7.4.9). No samples have been collected
directly at the head of the waterway to help determine if drains or runoff
in that area are potential contributors of copper.
Only a single sediment core sample was available from St. Paul Waterway.
In general, contaminant concentrations were similar in both the upper and
lower horizons (Table 7.4.1). For some of the contaminants of concern
(e.g., alkylated phenols), the similarity of concentrations throughout
the core may reflect mobility in interstitial water, a relatively constant
pattern of historical contaminant input, or constant in situ production
throughout the core. For relatively insoluble contaminants (e.g., copper),
the similarity of concentrations throughout the core suggests Input at
an approximately constant rate over the depositional period sampled by
the core.
7.4.3 Loading Estimates
Loadings of the contaminants of concern from all known discharges
to St. Paul Waterway are discussed below. The Puyallup River is treated
as a discharge because of the potential effect of riverine loading on sediment
quality in the adjacent St. Paul Waterway. Because of dilution and dispersion
of the Puyallup River plume, only a small portion of the river's total
contaminant load could affect sediment quality in St. Paul Waterway.
7.4.3.1 Organic Enrichment--
In order to Identify potential sources of the organic material in
the area of concern, available data on BOD, COD, and total suspended solids
(TSS) in discharges to St. Paul Waterway were compiled, as summarized in
Table 7.4.2. The Puyallup River is a major contributor of BOD, COD, and
TSS to Commencement Bay. Although the portion of this loading reaching
St. Paul Waterway 1s unknown, 1t is believed to be small. The Champion
International main outfall (SP-189) 1s the other discharge 1n the area
of concern known to be a significant source of organic matter.
7.4.3.2 Alkylated Phenols-
Analyses have not been done for 2-methyl or 4-methylphenol in the
Puyallup River or 1n any discharge to St. Paul Waterway. On eight occasions,
7.150
-------
Table 7.4.1
CONCENTRATION OF THE CONTAMINANTS OF CONCERN
WITH DEPTH IN THE SEDIMENT
STATION SP-60, BOl
Horizon la Horizon 2a
Contaminant (0-0.13 m) 0.13-0.30 m)
2-methyl phenol 91 b 89 b
4-methylphenol 3,900b 3,900 b
Naphthalene 1,490 2,010
2-methylnaphthalene 210 710
Copper 73 84
Total organic carbon 8.3% 11.8%
No data available for methoxyphenols or 1-methyl(2-methylethyl)benzene.
Concentrations given as ug/kg dry weight for organic compounds,
mg/kg dry weight for copper.
^Concentration exceeds toxicity or benthic AET.
7.151
-------
Table 7.4.2
BOD, COD, AND TOTAL SUSPENDED SOLIDS: SUMMARY OF LOADINGS FROM
DISCHARGES TO THE ST. PAUL WATERWAY AND FROM THE PUYALLUP RIVER9
Drain #
Drain Name
Flow (MGD)
(Avg. and Range)
(f of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)
B0D,a
PU-000
Lower Puyallup River
Mouth to Clear Creek
4044.2
(1,157-12.216)
(n-4)
8/25/81
11,000C
(6,000-18,000)
(n-3)
370,000
(200,000-610,000)
SP-189
Champion International
Mtln Outfall
32.2
(n-1)
8/11/81
26,000
(n-1)
7,000

C0Db
PU-000
Lower Puyallup River
Mouth to Clear Creek
4044.2
(1,157-12.215)
(n-4)
8/25/81-2/16/82
26,000
(9.000-40,000)
(n«5)
880.000
(300.000-1,300,000)
SP-189
Champion International
Main Outfall
32.2
(n-1)
8/11/81
500,000
(n-1)
130,000
TOTAL SUSPENDED S0LIDSb
PU-000
Lower Puyallup River
Mouth to Clear Creek
4044.2
(1,157-12,215)
(n-4)
8/25/81-2/16/82
380,000
(270,000-600,000)
(n-5)
12.000.000
(9,100,000-20,000,000)
SP-189
Champion International
Main Outfall
32.2
(n-1)
8/11/81
100,000
£1)
27,000
SP-268-01
St. Paul Storm Drain
0.129
(0.026-0.232)
(n-2)
6/29/84
260,000
(n-1)
280
SP-268-02
St. Paul Storm Drain
0.080
(0.043-0.116)
(n-2)
12/12/83-6/29/84
34,000
(16,000-52,000)
(«-2)
23
(11-35)
*The Puyallup River loading represent total loading to Comnencement Bay; loading to St. Paul Waterway considerably lower.
''From data 1n project data base only.
'Excluding WDOE Station 4 sampled 8/25/81 at high slack tide (Johnson and Prescott 1982b). This sample was collected <50 m
uprlver from Tacama Central STP outfall and 1s more representative of STP effluent than actual river water.
7.152
-------
ST. PAUL WATERWAY
the Puyallup River has been analyzed for 2»4-dimethylphenol. The compound
was not detected at a detection limit of 10 ug/l.
7.4.3.3 Naphthalene-
Naphthalene loading from discharges to St. Paul Waterway is summarized
in Table 7.4.3. The Champion International main outfall was the major
contributor (1.2 lb/day), based on a single analysis of their discharge
during the Class II survey (Yake 19B2b). Naphthalene has not been detected
in the Puyallup River (at a 10 ug/L detection limit), with the exception
of a single sample taken within 50 m of the Tacoma Central sewage treatment
plant (Johnson and Prescott 1982b). Based on the contaminant concentrations
in this sample relative to other river samples, the sample was probably
more representative of the treatment plant effluent rather than of Puyallup
River water which could impact St. Paul Waterway.
7.4.3.4 Methoxyphenols, 1 -Methyl (2 -methyl ethyl) benzene, and Methyl naphthalene-
No analyses have been done for these compounds in the Puyallup River
or in any discharge to St. Paul Waterway.
7.4.3.5 Copper-
Copper loadings from the Puyallup River and in discharges to St. Paul
Waterway are summarized in Table 7.4.3. The Champion International main
outfall effluent had the highest copper concentration of the known discharges,
although the Puyallup River was a greater source of mass loadings to Caimence-
ment Bay because of the high flaw volume of the river.
7.4.4 Source Identification
The highest concentrations (dry-weight basis) of all preliminary contami-
nants of concern were found at stations adjacent to the main outfall of
Champion International (SP-189). Discharges from the main outfall of Champion
International are therefore implicated as a major route by which contaminants
reach St. Paul Waterway. Some contaminants (1*e., copper and hydrocarbons)
may have additional sources elsewhere 1n the waterway.
The Champion International facility, recently purchased from St. Regis
Paper Company, is a softwood, kraft pulp and paper mill. Kraft pulping
involves the use of sodium hydroxide and sodium sulfide to dissolve lignin
from the wood so that the cellulose fibers can be separated. The facility
produces unbleached kraft lmerboard, unbleached kraft paper, bleached
paper, and bleached market pulp. Prior to 1970, untreated plant effluent
was discharged to the Puyallup River through discharge PU-190 shown in
Figure 7.4.1. In late 1970, primary clarification was initiated and the
discharge was routed to Its present location. Secondary treatment began
in 1977, Wastewater 1s presently treated by primary clarification, pure
oxygen activated sludge, and secondary clarification.
7.153
-------
Table 7.4.3
NAPHTHALENE AND COPPER: SUMMARY OF LOADINGS FROM
DISCHARGES TO THE ST. PAUL WATERWAY AND FROM THE PUYALLUP RIVER
Drain f
Drain Name
Flow (MGD)
(Avg. and Range)
(I of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(I of Observations)
Loading (lbs/day)
(Avg. and Range)
NAPHTHALENE
SP-189
Champion International
Main Outfall
32.2
(n»l)
8/11/81
4.4
(n-1)
1.2
SP-268-01
St. Paul Storm Drain
0.129
(0.026-0.232)
(n-2)
9/14/81
0.4
(n-1)
0.00043

COPPER
PU-000
Lower Puyallup River
Mouth to Clear Creek
4044.2
(1.157-12,215)
(n-4)
7/28/81-2/16/82
<16
(9-20)
(n-8)
<540
(304-675)
SP-189
Champion International
Main Outfall
32.2
(n-1)
8/11/81
100
(£l)
27
SP-268-01
St. Paul Storm Drain
0.129
(0.026-0.232)
(n-2)
9/14/81
10
(n-1)
0.01
SP-268-02
St. Paul Storm Drain
0.080
(0.043-0.116)
(n-2)
9/14/81
39c
(26-60)
(n-3)
0.026
(0.017-0.040)
SP-269
Ten-Inch Corrugated
Pipe
0.012
(n-1)
8/12/81
20
£1)
0.0020
aThe Puyallup River loadings represent total loading to Commencement Bay; loading to St. Paul Waterway considerably lower.
Excluding MDOE Station 4 sampled 8/25/81 at high slack tide (Johnson and Prescott 1982b). This sample was collected <50 m
uprlver from Tacoma Central STP outfall and Is more representative of STP effluent than actual river water.
'Concentration corrected for contribution of blank.
7.154
-------
ST. PAUL WATERWAY
As discussed in Section 7.4.3, only three of the seven preliminary
contaminants or contaminant groups of concern have been detected in the
Champion International effluent (naphthalene, copper, BOO). The effluent
has not been analyzed for the other preliminary compounds of concern, but
they could be associated with effluent from a pulp and paper mill. Each
is discussed below with regard to known or potential presence in the Champion
International effluent.
Chloroform was detected at elevated concentrations in 1981 analyses
Johnson and Prescott 1982c) of the plant effluent and receiving water,
hloroform was undetected at 10 ug/kg dry weight in samples from the three
sediment stations analyzed for chloroform during the remedial investigation.
These stations included Station SP-14 directly off the main outfall.
7.4.4.1 Organic Enrichment--
Pulp and paper mills have traditionally been of concern in water pollution
abatement programs because of their discharge of suspended solids and oxygen-
consuming materials. Activated sludge digestion and secondary clarification
are designed to reduce the BOD/COD content of the Champion International
effluent. However, even with this treatment, the outfall contributes 7,000
lb/day BOD and 130,000 lb/day COD. BOD limits of 7,300 lb/day daily average
and 14,400 lb/day daily maximum are Included 1n the firm's NPDES permit.
Therefore, it is not surprising that the marine sediments near the outfall
are organically enriched.
7.4.4.2 Alkylated Phenols--
2-Methylphenol (unidentified isomer), produced by cleavage of the
lignin molecule, is frequently found in pulp mill effluents (LaFleur, L.,
personal communication). Although 4-methylphenol (p-cresol) has been reported
as a constituent in pulp mill effluent (Nestmann et al. 1980), its presence
is not typical. However, it is possible that 4-methyl phenol is produced
by anaerobic microbial breakdown of lignin.
Sediments in the vicinity of the Champion International outfall contained
concentrations (dry weight) of 4-methyl phenol that were two orders of magnitude
greater than those from any other site 1n the nearshore/tideflats area.
2-Methylphenol was undetected In the sediments nearest the outfall. Therefore,
alkylated phenols 1n the area of concern may originate from in situ microbial
degradation of pulp processing wastes discharged from the Champion International
outfal1.
The degradation of wood chip debris in sediments 1s a possible source
of alkylated phenols. The presence of wood or woody material In Commencement
Bay sediments was checked through a review of grain size records for samples
collected in March, 1984. Wood debris was noted 1n surface sediments from
89 stations that contained measurable quantities of 4-methyl phenol. This
group of stations Included Stations SP-14 and SP-15 near the main outfall
of Champion International. 4-Methylphenol was undetected at 10 ug/kg (dry
weight) in sediments from an additional nine stations where wood debris
7.155
-------
ST. PAUL WATERWAY
was also noted (including two stations from Carr Inlet). Finally, 4-methyl-
phenol was found at an average value of 170 ug/kg (maximum 890 ug/kg dry
weight at Station SP-16) in sediments from 16 stations where no wood debris
was reported in the grain size analyses. Although wood content could only
be qualitatively estimated, there was no obvious correlation in the amount
of wood debris suggested by grain size records and the concentration of
4-methylphenol in any of the sediment samples evaluated.
Degradation of wood debris (as opposed to pulping wastes contributed
by effluents) is unlikely to account for the 96,000 ug/kg dry weight concen-
tration observed in sediment from Station SP-14 off the main outfall of
Champion International. Considerable wood debris was noted in sediment
from Station CI-16 in Wheeler-Osgood Waterway. In fact, sediment coring
in Wheel er-Osgood Waterway was difficult because of wood debris. The maximum
concentration of 4-methylphenol in this organically enriched, anoxic basin
was 1,200 ug/kg, approximately one percent of the concentration observed
at Station SP-14. Other potential sources besides wood debris were also
identified in Wheel er-Osgood Waterway. It was concluded that degradation
of wood debris may contribute a portion of the 4-methyl phenol observed
in some sediments. Other processes (i.e., the direct discharge of 4-methyl-
phenol or degradation of some effluent component) appear to be of greater
importance in St. Paul Waterway.
7.4.4.3 Methoxyphenols--
2-Methoxyphenol (guaiacol) is a major constituent in pulp mill effluents,
because lignin consists of numerous propylguaiacol building blocks and
guaiacol is one of the major products of lignin breakdown (Fox 1977).
Of 48 constituents of pulp mill effluent identified by Nestmann et al. (1980),
2-methoxyphenol was present 1n the greatest concentrations (3 mg/L). It
was also one of 16 major components identified by Fox (1977) from a pulp
and paper mill on Lake Superior. No analyses were reported for this compound
in the Champion International effluent. Since the compound 1s characteristic
of the pulp and paper production, it is probable that it is entering the
waterway via the main outfall.
7.4.4.4 1-Methyl(2-methyl ethyl)benzene--
l-Methyl-2-(methylethyl)benzene (tentative Identification; commonly
known as p-cymene) 1s a common component of sulfite mill waste liquors
and has also been identified in the effluent from a kraft mill (Rogers
et al. 1982). l-Methyl-2-(methylethyl)benzene, an alkylated benzene, is
formed by the dehydration of monocyclic terpenes. These terpenes can be
made from turpentine or obtained as a by-product from sulfite digestion
of spruce pulp (Hawley 1981). Neither Champion International nor St. Regis
has employed sulfite digestion 1n pulp and paper production. Alkylated
benzenes derive from numerous sources not restricted to the pulp and paper
industry. However, given the association of alkylated benzenes with the
pulp and paper Industry, and the high concentration of compounds observed
1n sediments near the Champloin International outfall, this class of compounds
is probably present 1n the Champion International effluent. An alkylated
7.156
-------
ST. PAUL WATERWAY
benzene isomer has also been tentatively identified in the sediments near
the plant's pre-1970 outfall on the Puyallup River (Yake 1982b).
7.4.4.5 Naphthalene and 2-Methylnaphthalene—
Naphthalene and methyl naphthalenes are occasionally seen as trace
constituents in pulp and paper mill effluents, although they are usually
not typical or major components (Wall in and Condren 1981). The Champion
International effluent has been found to contain 4.4 ug/L naphthalene (Yake
1982b). Regulatory limits for naphthalene concentrations that induce chronic
effects on saltwater organisms have not been established. The saltwater
criterion for acute effects is 2,350 ug/L. The origin of naphthalene in
the Champion International waste stream is not known. The compound is
used as a fungicide (Hawley 1981) and may be used in small quantities in
paper manufacturing.
7.4.4.6 Copper--
The Champion International effluent is a known source of copper, con-
tributing 27 lb/day to Commencement Bay and St. Paul Waterway (Table 7.4.2).
Water samples taken in Commencement Bay near the plant outfall contained
47 ug/L copper, twice the U.S. EPA maximum allowable concentration for
saltwater (Johnson and Prescott 1982c). Copper is not a typical constituent
of pulp and paper mill effluent. It is not clear why the metal is present
in significant quantities in the Champion International effluent, although
the NPDES permit recently issued to Champion International requires the
firm to perform in-plant testing to determine the copper source. The WDOE
is currently investigating the possibility that use of "Raffinate" at Champion
International may be a source of copper. "Raffinate" is a black liquor
high in sodium purchased by Champion International for use as salt cake
make-up. The product contains 120 mg/kg copper (Fenske, F., personal
communication).
The distribution of copper in surficlal sediments 1s shown in Figure
7.4.9. The highest concentration (275 mg/kg dry weight) was found near
the present location of the Champion International outfall. It is significant
that the second highest concentration shown (180 mg/kg) was found off discharge
PU-190, the site of the facility's previous outfall. Thus, high copper
concentrations 1n sediment appear 1n both locations where plant effluent
has been discharged. The PU-190 discharge was probably a significant source
of copper prior to 1970, and only a periodic source during emergency plant
bypasses since that time. The main plant outfall, SP-189, continues to
be a major ongoing source of copper. Uniformly elevated copper concentrations
throughout the SP-60 sediment core also support long-term input of copper.
Based on contaminant gradients, the known or potential presence of
all contaminants of concern 1n the Champion International effluent, and
a preliminary assessment of mass fluxes of some contaminants, the firm's
main outfall appears to be the source of the contamination observed in
samples from Stations SP-13 through SP-16. Given the proximity of the
Puyallup River to the area of concern at the mouth of St. Paul Waterway,
7.157
-------
ST. PAUL WATERWAY
deposition of contaminated, river-borne particulates may contribute to
the contamination. However, this contribution is not likely major because
of the following reasons:
• The contaminants that have elevated concentrations in the
area of concern have either been found in the Champion Inter-
national effluent or can be associated with the pulp and
paper industry 1n general. There are no substances showing
elevated concentrations whose presence could be attributable
only to an alternative source.
• Copper is introduced via the Champion International effluent.
It has been found at 100 ug/L in the effluent and at elevated
concentrations in sediments from the two areas where effluent
has been discharged. The similarity of the copper distribution
in the surficial sediments with the distributions of the
other compounds suggests that the effluent 1s a source for
all of the contaminants of concern.
• 2-Hethoxyphenol (guaiacol) is a degradation product of lignin
and thus is a good indicator of pulp and paper mill effluent.
It has been tentatively identified in the effluent of the
Tacoma Central sewage treatment plant at a concentration
of 5 ug/L (Yake 1982c). Given the dilution of the treatment
plant effluent by the Puyallup River (approximately 100:1)
and the further dilution of the Puyallup River upon reaching
Commencement Bay, it is unlikely that the Puyallup River
is a significant source of this compound to this waterway.
• Coprostanol is an indicator of contamination by mammalian
fecal material. Coprostanol concentrations in the sediments
of St. Paul Waterway are the highest reported 1n the near-
shore/tideflats area (up to 2,800 ug/kg at Station SP-11
near the head of the waterway), potentially because of the
influence of the Puyallup River. The St. Paul Waterway
station with the highest concentrations of the contaminants
of concern (SP-14) had undetected concentrations of coprostanol.
Therefore, if the Puyallup River is a major source of the
coprostanol, and no coprostanol was found at the site of
greatest contamination, the Puyallup River is unlikely to
be the major source of that contamination (I.e., at Station
SP-14).
• The Puyallup River plume can be expected to affect sediment
quality to the north of the river mouth (Sltcum and Milwaukee
Waterways) at least as much as areas to the south (St. Paul
Waterway). Therefore, if the Puyallup River were the major
source of the contaminants of concern, their concentrations
1n Sitcum and Milwaukee Waterways should be at least as
great as those 1n St. Paul Waterway. Because this is not
the case (with the exception of copper 1n Sitcum Waterway
7.158
-------
ST. PAUL WATERWAY
likely derived from local sources), the Puyallup River does
not appear to be the major source of the contamination observed
in St. Paul Waterway.
7.4.5 Summary and Recommendations
Champion International is implicated as the major source of all preliminary
contaminants of concern in St. Paul Waterway. The proximity of the most
contaminated sediments to the firm's main outfall indicates that this discharge
is the route of contaminant input. The BOD/COD discharge is ongoing, and
chemical analyses of the effluent (1981 Class II survey) indicated that
discharge of at least naphthalene, chloroform, and copper was ongoing at
that time. There is no reason to believe that the presence of any of the
contaminants of concern is strictly a result of historical discharge.
Efforts should be directed toward reducing or eliminating discharge
of the contaminants of concern via the Champion International main outfall.
Because this is an NPDES-permitted discharge, the NPDES program should
provide the mechanism to accomplish this goal. Further impetus for regulation
is provided by the fact that U.S. EPA water quality criteria for copper
are violated in the vicinity of the outfall, and that significant bioaccumu-
1 at ion of copper was found in English sole from St. Paul Waterway. Without
source control, removal of contaminated sediments presently in the bay
or St. Paul Waterway cannot be justified for other contaminants. Source
control alone would probably be adequate to reduce dramatically sediment
contamination by naphthalene and 4-methylphenol. Given the solubility
of these compounds, they would not be expected to persist In the sediments
if the effluent source were eliminated. On the other hand, if alkylated
phenols are produced by 1n situ degradation of pulping waste products or
wood chip debris burled in the sediments, there may be continued high levels
for a considerable period of time. Copper would also be expected to persist
in the sediments for many years even if source control were initiated.
This is demonstrated by the elevated copper concentrations that have persisted
at the pre-1970 Puyallup River outfall site.
7.159
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7.5 MIDDLE WATERWAY
7.5.1 Introduction
Middle Waterway was created prior to 1923 (Hart-Crowser and Associates
undated). With minor exceptions, the waterway remains unchanged from its
original configuration. Unlike the other waterways in the tideflats, much
of Middle Waterway (approximately the upper half) remains intertidal.
Several industries are located along the waterfront, as shown in Figure
7.51. On the east side, Paxport Mills operates a sawmill that produces
cedar fencing and alder paneling. The remainder of the waterfront on the
east peninsula south of Paxport Mills is occupied by Champion International,
formerly St. Regis Paper Company. It was originally the location of the
St. Paul and Tacoma Lumber Company, which opened a mill in the area in
1889 (Morgan and Morgan 1984).
Other industries that used to be located on or around Middle Waterway
include several foundries and metalworking companies, three oil companies,
three lumber companies, two maritime industries, and a coal products manu-
facturer. There are also references to a facility using creosote for timber
treatment in the 1910s. No further information is available on any of
these historical industries.
Middle Waterway 1s bordered on the south by 11th Street and two bus-
inesses: Washington Belt and Drive, and Western Machine. Pacific Yacht
Basin, a fire station, and a utility substation occupy the southwest corner
of the waterway. Coast Craft, a custom woodworking firm, occupies the
southern shoreline near the head of the waterway. The remainder of the
western shoreline is occupied by maritime industries including Foss Launch
and Tug (a Dillingham Maritime Company), Marine Industries Northwest, and
Cook's Marine Specialties.
There has been only one dredge and fill project within the waterway
since 1970. In 1982 Paxport Mills reset a seawall and filled an area on
the east side of the waterway to provide additional storage area for hog
fuel. Approval of this project by the Corps of Engineers and WDOE was
contingent upon the development of a salmon enhancement area near the mouth
of Middle Waterway along the northwest shore. This enhancement area would
replace the Intertidal area that was destroyed when Paxport constructed
their hog fuel storage area. Under the terms of the permit (071-0YB-2-
006450-R), this area was to receive clean fill and clean dredge spoils.
Instead, Paxport used wood wastes mixed with ASARCO slag as the fill material.
The U.S. EPA and the Corps of Engineers plan to take enforcement action
against Paxport, and WDOE has withdrawn their approval of the project
(Ruckelshaus, M., 2 August 1985, personal communication). Other dredging
projects Include Puget Sound Plywood located at the end of the peninsula
separating Middle and City Waterways 1n 1972 and 1978 to deepen the channel
near their mill.
7.160
-------
St. Paul Waterway
Champion
International
Paxport Mills
Middle Waterway
Foss Tug
Coast Craft
Marine Industries Northwest
Power
Substatio
Puget Sound
Plywood
D-Street Petroleum
Facilities
(multiple owners)
Foss/
D111ingham
Cooks
Marine
Specialties
Washington
"Belt & Drive
™-200,, .
^--Western
Machine
^{disconnected)
Pacific
Yacht Basin
Fire Station
Figure 7.5.1
MAJOR INDUSTRIES AND DISCHARGES TO THE MIDDLE WATERWAY
INDUSTRY BOUNDARIES APPROXIMATE, BASED ON DRIVE-BY INSPECTION
-------
MIDDLE WATERWAY
There are no NPDES-permitted discharges to Middle Waterway. The largest
outfall is a 27-in storm drain (MD-200) that discharges at the head of
the waterway.
Locations of sediment chemistry stations in Middle Waterway are shown
in Figure 7.5.2, including those sampled as part of the Superfund investigation
and all historical sampling sites. Preliminary contaminants or contaminant
groups of concern in Middle Waterway include
Organic Compounds
Pentachlorophenol
Dichlorobenzenes
Aromatic hydrocarbons
Dibenzofuran
Inorganic Substances
Copper
Mercury
The spatial distributions, known loadings, and potential sources of these
compounds are discussed below. Concentrations of these preliminary contaminants
of concern were later determined to exceed toxicity or benthic AET in sediments
from at least one station in Middle Waterway. Other substances that were
present above AET at a single station only (Priority 3 chemicals; see Table
6.14 in Section 6) but for which sources have not yet been evaluated include
Substance Station Where AET Exceeded
Phenol MD-11
4-Methylphenol MD-13
Arsenic MD-13
Zinc MD-01
Except phenol, concentrations of these substances exceeded AET only when
normalized to percent fine-grained material. Additional tentatively identified
substances include dibenzothiophene (Station MD-11), methylpyrenes (Station
MD-01), and two diterpenoid hydrocarbons (Station MD-01). Except dibenzo-
thiophene, these compounds exceeded AET only when normalized to percent
fine-grained material. These lower priority substances are not discussed
further.
Average mass flux estimates were calculated only for copper and mercury
in Middle Waterway. Source data for other contaminants were Insufficient
for analysis. Mass flux estimates for copper and mercury were evaluated
using average concentrations of these contaminants 1n sediments from all
present and historical stations according to the procedures and criteria
outlined in Section 2.12.3.2. The source-derived mass flux for both metals
was less than 1 percent of the sediment concentration-derived mass flux.
According to the uncertainty criteria for this analysis, a data gap in
the identification of copper and mercury sources is indicated. This conclusion
is reasonable given that the highest sediment concentrations were observed
at the opposite end of Middle Waterway from the MD-200 outfall, the only
established source of copper and mercury.
7.162
-------
^MD-199
T— MD-200
HD-201
(disconnected)
--01
M ° • BMD-12
MD"13 MD-19
A-2
MD-220
300 600
Sediment
Core MD-60
~ Tetra Tech
A EPA
X Other Agencies
METERS
Figure 7.5.2
SURFIC1AL SEDIMENT STATIONS AND SEDIMENT CORE LOCATIONS
FROM ALL STUDIES IN MIDDLE WATERWAY
7.163
-------
MIDDLE WATERWAY
7.5.2 Pentachlorophenol and Dichlorobenzenes
7.5.2.1 Spatial Distribution-
Concentrations of several organic compounds decreased along the length
of Middle Waterway, with sediment concentrations at the head of the waterway
several times greater than those at the mouth. These compounds included
1,2-dichlorobenzene, 1,4-dichlorobenzene, 1,2,4-trichlorobenzene, phenol,
alkylated phenols, and pentachlorophenol. Of these, pentachlorophenol
and the dichlorobenzenes are of concern. Concentrations of pentachlorophenol
and 1,4-dichlorobenzene in the surficial sediments of Middle Waterway are
shown in Figures 7.5.3 and 7.5.4.
Sediment contaminant data were collected at only a few stations in
Middle Waterway. Therefore, evaluation of spatial gradients is limited.
For both pentachlorophenol and 1,4-dichlorobenzene, the highest dry-weight
concentrations were measured in the intertidal area near the head of the
waterway. Upper Middle Waterway is an intertidal depositional environment
and organic carbon levels are higher in surficial sediments than in deeper
sediments. The available data are not sufficient to determine whether
the observed levels of pentachlorophenol and 1,4-dichlorobenzene result
from sources near the waterway head, or from transport and deposition of
contaminated sediments originating elsewhere in the waterway.
A single sediment core sample was taken near the mouth of Middle Waterway
(Station MD-60). Pentachlorophenol and dichlorobenzene concentrations
(ug/kg dry weight) within this core were
Pentachlorophenol 1,2-Dichlorobenzene 1,4-Oichlorobenzene
Horizon 1 undetected at 25 10.8 29.7
(0-0.13 m)
Horizon 2 undetected at 50 undetected at 5 undetected at 5
(0.13-0.32 m)
These data indicate that dichlorobenzene input is either recent or ongoing.
The pentachlorophenol detection limits were too high to draw any conclusions
regarding contaminant input over time for this compound. None of these
concentrations exceed AET.
7.5.2.2 Loading Estimates--
There are three discharges at the head of Middle Waterway: a seep
(MD-199), a 27-in storm drain (M0-200), and a 4-1n PVC pipe (MD-201).
Only MD-200 effluent has been analyzed for pentachlorophenol or dichloro-
benzene. This discharge was analyzed on three occasions between April,
1982 and May, 1984 and in all cases was found to contain undetectable concen-
trations of both pentachlorophenol and the dichlorobenzenes (W00E unpublished).
Detection limits ranged from 1 to 10 ug/L.
7.164
-------
(A)

^ MD-199
J— MD-200
^ MD-201
(disconnected)
620
u740
MD-220
AET not established
(B)
mg/kg TOC
mo-w
1—— MD-200
MD-201
(disconnected)
MD-220
~ Tetra Tech
A CPA
METERS
160
AET not established
Figure 7.5.3
CONCENTRATIONS OF PENTACHLOROPHENOL IN THE
SURFICIAL SEDIMENTS OF MIDDLE WATERWAY
7.165
-------
HD-220
(A)
pg/kg dry weight
MO-199
MD-200
M0-201
(disconnected)

~ Exceeds benthlc effects and toxicity AET of 120 ug/kg DW
(B)
mg/kg TOC
MD-220
HD-199
— MD-200
M0-201
(ditCOIMMCUd)
~ Tetra Tech
0 150
No organic carbon normalized AET exceeded
Figure 7.5.4
CONCENTRATIONS OF 1,4-DICHLOROBENZENE IN THE
SURFICIAL SEDIMENTS OF MIDDLE WATERWAY
7.166
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MIDDLE WATERWAY
7.5.2.3 Source Identification--
The spatial distributions of pentachlorophenol and dichlorobenzenes
in the surficial sediments of Middle Waterway suggest at least one source
at the head of the waterway. No known discharge to Middle Waterway contains
either pentachlorophenol or dichlorobenzenes, but potential sources can
be identified in order to aid further investigative activity.
Pentachlorophenol is a bactericide, fungicide, and slimicide used
primarily for wood preservation (U.S. EPA 1980b). There are two wood products
industries in the tideflats area from which a discharge would reach the
head of Middle Waterway: Champion International and Coast Craft. Champion
International is located along the eastern shore of Middle Waterway. Runoff
from the Champion International log storage, debarking, and sawing areas
could reach the head of Middle Waterway via the MD-200 storm drain. Dames
and Moore (1982) noted that prior to 1975-76, a "Permatox" dip tank was
maintained on site. "Permatox" is a fungicide and anti-stain agent containing
mercury and tetra- and/or pentachlorophenate salts. The pentachlorophenate
salt would not be expected to be transformed to pentachlorophenol at pH
conditions typical of the marine environment (Schellenberg et al. 1984).
Therefore, "Permatox" is not considered to be the source of the pentachloro-
phenol observed in Middle Waterway. However, the types and volumes of
preservatives used by Champion International since 1976, if any, have not
been established. The WDOE is unaware whether wood preservatives are currently
in use on-site (Fenske, F., personal communication).
Coast Craft is located at 1002 East F Street at the head of Middle
Waterway along the western shore. The firm performs custom woodworking
and treats lumber with wood preservatives. In the Tacoma Tideflats Industrial
Survey conducted by the Pierce County Health Department, it was reported
that Coast Craft had a pentachlorophenol dip tank (Pierce, R., 15 July
1985, personal communication).
There is no documented source of dichlorinated benzenes to Middle
Waterway. Therefore, source Identification efforts must focus on uses
of the compounds. The uses of 1,2-dichlorobenzene include (Hawley 1981)
• Solvent for a wide range of organic materials
t Solvent for nonferrous metals
• Degreasing of hides and wool
• Metal polishing
• Industrial odor control
• Dye manufacturing
7.167
-------
MIDDLE WATERWAY
• Production of 3,4-dichloroaniline and toluene diisocyanate
t Heat transfer.
1,4-Dichlorobenzene is used as an air deodorant and an insecticide, which
account for 90 percent of its total production (U.S. EPA 1980c).
No single major source of these contaminants to Middle Waterway can
be identified based on these uses. The shoreline surrounding the head
of the waterway is occupied by Coast Craft (custom woodworking) to the
west, piles of sawdust from Champion International to the east, and Pacific
Yacht Basin, a marine supply store, at the southern end. None of these
sites appears to be a likely source of the chlorinated benzenes. The drains
and seeps at the head of the waterway are possible sources. The MD-200
storm drain has the largest flow volume of these discharges. Based on
a review of drainage maps provided by Tacoma-Pierce County Health Department
and the Tacoma Department of Public Works, this drain serves East 11th
Street (from East F Street to Portland Avenue) and Portland Avenue (from
East 11th Street to 0.7 km east of the llth/Portland intersection). Most
of this area is occupied by Champion International. Discharge MD-201,
a 4-in pipe from Pacific Yacht, has been abandoned, and the origin of the
MD-100 seep is unknown.
7.5.2.4 Summary and Recommendations--
Highest sediment concentrations of both pentachlorophenol and the
dichlorinated benzenes were measured near the head of Middle Waterway,
indicating the possible presence of a source in this area. Although there
has been no documented discharge of pentachlorophenol or dichlorinated
benzenes to the waterway, Champion International (formerly St. Regis) and
Coast Craft are potential sources of pentachlorophenol, based on the use
of the compound in the wood products industry and the fact that discharge
from the facilities can reach the head of Middle Waterway either directly
or via the storm sewer network. The presence of pentachlorophenol in surface
sediments indicates that contamination is either recent or ongoing. Input
of dichlorinated benzenes appears to be either recent or ongoing. The
ultimate source of the compounds could not be Identified.
The following recommendations can be made based on source identification
efforts:
t The use of wood preservatives at Coast Craft and Champion
International should be Investigated. In particular, it
should be established whether pentachl orophenol-based preserva-
tives have been used, whether this use 1s continuing, and,
if it is, whether the compound may be entering the waterway.
• Sediment samples at the discharge points of MD-199 and 200
should be taken and analyzed for chlorinated benzenes.
Once the source discharge 1s Identified, the drainage area
should be delineated and appropriate industries investigated
7.168
-------
MIDDLE WATERWAY
for the potential use and discharge of products containing
dichlorinated benzenes.
• More surface sediment sampling should be conducted to allow
better spatial resolution of distributions of pentachlorophenol
and dichlorinated benzenes.
• A subsurface core should be taken at the head of the waterway.
7.5.3 Aromatic Hydrocarbons and Dibenzofuran
7.5.3.1 Spatial Distribution-
Distributions of polycyclic aromatic hydrocarbons (PAH) and dibenzofuran
in surficial sediments of Middle Waterway are shown in Figures 7.5.5-7.5.7.
LPAH, HPAH, and dibenzofuran all displayed similar distributions. Samples
from Station MD-01, located approximately midway along the length of the
waterway, had the lowest concentrations on a dry-weight basis. These low
concentrations were probably a consequence of the coarse sediments and
low organic content of these sediments, since when normalized to organic
carbon, concentrations at this station were comparable to others in the
vicinity. Dry-weight concentrations of LPAH, HPAH, and dibenzofuran were
somewhat lower at the mouth of the waterway (MD-13) than at the head of
the waterway. However, after normalization to organic carbon, the concentra-
tions were highest near the mouth (e.g., Station MD-12). Lower concentrations
at stations outside Middle Waterway and directly at the waterway mouth
(i.e., Station MD-13) suggested that contaminants were not advected from
the bay into the waterway. Beyond this, there was no clear gradient of
contamination with which to establish the location of potential sources.
As shown below, PAH concentrations in the sediment core sample taken
near the mouth of the waterway station (MD-60) were slightly higher in
the lower horizon than 1n the upper horizon, suggesting a slight decrease
in the rate of contaminant input in recent years. Dibenzofuran concentrations
were approximately equal in the two horizons sampled. These values are
comparable to the concentration of LPAH and dibenzofuran in surface sediments
from Middle Waterway. HPAH concentrations were twice as high in the sediment
core samples than in the surface sediments.
LPAH HPAH Dibenzofuran
(ug/kg DW) (ug/kg DW) (ug/kg DW)
Horizon 1
(0-0.13 m) 5,300 15,300 480
Horizon 2
(0.13-0.32 m) 7,300 16,700 470
LPAH and HPAH concentrations 1n the core exceeded AET. The dibenzofuran
concentrations did not exceed AET.
7.169
-------
A
L1600
HD-220
(A)
pg/kg dry weight
*6700
HD-199
—-»-200
MD-201
(diiconnected)
V,
>»
~ Exceeds AET (see Table 4.2 for AET values)
MD-220
(6)
mg/kg TOC
MD-199
H0-200
m-201
(d<(connected)
METERS
~ Tetra Tech
A EPA
X Other Agendas
No organic carbon normalized AET exceeded
(sm Table 4.6 for AET values)
Figure 7.5.5
CONCENTRATIONS OF LOW MOLECULAR WEIGHT PAH IN THE
SURFICIAL SEDIMENTS OF MIDDLE WATERWAY
7.170
-------
A
3500
f
MD-220
(A)
pg/kg dry weight
1°
L4100
MD-199
*13000>)cr M0*Z0°
n HD-201
(disconnected)

~ Exceeds AET
(see Table 4.2 for AET values)

(B)
mg/kg TOC
2i°
300
MD-220
METERS
MD-199
- MD-200
ND-201 ,
(disconnected)
~ Tetra Tech
A CPA
X Other Agencies
0 150
No organic carbon normal1zed AET exceeded
Figure 7.5.6
CONCENTRATIONS OF HIGH MOLECULAR WEIGHT PAH IN THE
SURFICIAL SEDIMENTS OF MIDDLE WATERWAY
7.171
-------
— MD-220
(A)
pg/kg dry weight
MD-199
— MD-200
M0-201
(disconnected)
'X
No dry weight normalized AET exceeded
(B)
mg/kg TOC
MD-220
HD-199
-H0-200
> HD-201
(dliconnected)
METERS
o Tetra Tech
0 150
No organic carbon normalized AET exceeded
Figure 7.5.7
CONCENTRATIONS OF DIBENZOFURAN IN THE
SURFICIAL SEDIMENTS OF MIDDLE WATERWAY
7.172
-------
MIDDLE WATERWAY
7.5.3.2 Loading Estimates--
The only discharge to Middle Waterway that has been analyzed for PAH
is MD-200. The effluent from this drain was analyzed three times between
April, 1982 and May, 1984. No PAH were found at detection limits ranging
from 0.1 to 10 ug/L (WDOE unpublished). Dibenzofuran analyses were performed
twice in the spring of 1984. On both occasions, the compound was undetected
at 0.1 ug/L.
7.5.3.3 Source Identification--
Source identification efforts were complicated by the absence of
clear gradients of PAH and dibenzofuran contamination along the length
of the waterway. If, as suggested by the highest concentrations of PAH
at the head of the waterway, the storm sewer represents the greatest con-
tributor (dry-weight basis), then efforts to locate the ultimate source
should focus on the drainage area served (see Section 7.5.2.3). The high
contaminant concentrations observed on a normalized basis within the central
portion of the waterway could have originated from the ship repair facilities
along the western shore. There is no known documented release from these
facilities based on a review of WDOE Environmental Complaint files, 1978-
1985. However, a long-term, chronic discharge of PAH may be expected from
runoff and activities such as bilge pumping.
7.5.3.4 Summary and Recommendations—
A major source for PAH could not be clearly established. These compounds
are ubiquitous in highly industrialized areas such as Commencement Bay,
and sources such as spills and bilge pumpage are not possible to quantify.
Further source identification efforts will require more intensive sediment
sampling to better define gradients of contamination suggested by the limited
data available. Additional sampling of discharges to Middle Waterway is
recommended.
7.5.4 Mercury and Copper
7.5.4.1 Spatial Distribution-
Concentrations of copper and mercury in the surficial sediments of
Middle Waterway are shown in Figures 7.5.8 and 7.5.9, using data from the
Tetra Tech 1984 survey and all available historical data. The highest
concentrations normalized to both dry-weight and to percent fine-grained
material were found at the mouth of the waterway (Station MD-13). The
decrease in metal concentrations with distance up the waterway, particularly
apparent for mercury, suggests that a source 1s located near the waterway
mouth.
A single sediment core sample was taken near the mouth of the waterway
within 100 m of the area of greatest surficial sediment contamination.
Copper and mercury concentrations (mg/kg) were as follows:
7.173
-------
A
100
S
*490
MD-220
(A)
mg/kg dry weight
MD-199
— MD-200
HD-201
(disconnected)
kl iim V ^
~Exceeds AET (see Table 4.1 for AET values)
(B)
mg/kg fines
MD-199
MD-200
^ HD-201
(dUconntcUd)
5$°
*890
~
*2300
MD-220
METERS
~ Tetra Tech
A EPA
X Other Agencies
0 150
*Excecds AET (see Table 4.8 for AET values)
Figure 7.5.8
CONCENTRATIONS OF COPPER IN THE
SURFICIAL SEDIMENTS OF MIDDLE WATERWAY
7.174
-------
(A)
mg/kg -dry weight
*0.67
HD-220
MD-199
i—- MD-200
NO-201
(disconnected)
X..
'X
~Exceeds AET (see Table 4.1 for AET values)
(B)
mg/kg fines
MD-220
METERS
MD-199
i— HO-200
^ MD-201
(disconnected)
~ Tetra Tech
A CPA
X Other Agencies
0 150
#Exceeds AET (see Table 4.8 for AET values)
Figure 7.5.9
CONCENTRATIONS OF MERCURY IN THE
SURFICIAL SEDIMENTS OF MIDDLE WATERWAY
7.175
-------
MIDDLE WATERWAY
Copper
Mercury
Horizon 1
(0-0.13 m)
435
4.2
Horizon 2
(0.13-0.32 m)
126
0.8
These data indicate that recent metal input, represented by Horizon 1,
is 3.5 to 5 times greater than historical Input, represented by Horizon 2.
Concentrations of copper exceeded AET only in Horizon 1. Mercury concentrations
exceeded AET in both horizons.
7.5.4.2 Loading Estimates--
MD-200 is the only discharge to Middle Waterway for which the effluent
has been analyzed for copper or mercury. Based on a flow of 0.3 MGD and
a copper concentration of 30 ug/L measured in the effluent in April, 1982
(W00E unpublished), a copper loading of 0.0075 lb/day can be estimated.
The estimated mercury loading from the drain was 0.000053 lb/day, based
on detection of 0.21 ug/L in April, 1984 (WD0E unpublished).
7.5.4.3 Source Identification--
The spatial gradient of metals contamination In the surficial sediments
of Middle Waterway suggests that the source of the metals is located near
the mouth of the waterway. A gradient of decreasing concentrations with
distance from the mouth could be the result of contaminant input from Commence-
ment Bay. However, this does not appear to be the case since similar upwaterway
gradients should be apparent in other waterways but are not. Decreasing
metals concentrations with distance from the mouth were apparent only for
Middle Waterway. Therefore the source is apparently unique to the waterway.
Champion International, known to be a source of copper to St. Paul
Waterway, may also be the major source of copper to Middle Waterway. However,
this hypothesis does not appear reasonable for three reasons. First, copper
concentrations were higher in Middle waterway by a factor of two than observed
1n any St. Paul Waterway sediment. Second, there was no consistent gradient
of copper concentrations between the two waterways (compare Figure 7.5.8
with Figure 7.4.9 1n Section 7.4). Third, mercury, as well as copper,
showed increased concentrations at the mouth of Middle Waterway, yet Champion
International is not known to be a significant source of mercury, and elevated
mercury concentrations occurred only 1n Middle Waterway sediments.
The most probable explanation for the observed pattern of contamination
1s the presence of a source near the mouth of Middle Waterway. Paxport
Mills Is located on the east shore of the waterway near the mouth. Release
of metals would not be expected since the firm 1s a sawmill and would not
typically handle metal-contaminated products. Paxport recently used a
mixture of wood wastes and ASARC0 slag to fill a salmon enhancement area
adjacent to their property near the mouth of the waterway. This project
7.176
-------
MIDDLE WATERWAY
was completed in 1982. Sediment samples were not collected from this area.
As discussed below, the relative concentrations of arsenic and copper in
sediments near the mouth of Middle Waterway were not consistent with those
found in ASARCO slag.
The western shoreline of the lower waterway is occupied by three maritime
industries (Cook's Marine Specialties, Foss Tug, and Marine Industries
Northwest) , each of which is involved in ship repair. A shipbuilding firm
has been implicated as a source of metals to City Waterway because of the
use and disposal of sandblasting grit in the waterway. Ship repair facilities
in southern California are major sources of copper and other metals because
of their use of metal-based antifouling paints (Young et al. 1979). Therefore,
ship repair facilities along the western shore of Middle Waterway may be
the source of the metals observed 1n Middle Waterway sediments. There
are too few sampling sites in the waterway to conclusively determine whether
this is the case. However, this determination could probably be made with
additional sampling data.
Sandblasting grit is one potential source of metals from ship repair
facilities. Up through the 1970s, ship repair firms in the tideflats area
typically used ASARCO slag for sandblasting. Its use has been documented
at Peterson Boat Building (Dames and Moore 1982), which occupied (until
1981) the property now owned by Cook's Marine Specialties. Ship repair
firms have since switched to commercially available sandblasting preparations,
such as "Tuf-Kut". In order to determine if sandblasting grit is responsible
for the metals contamination observed in Middle Waterway, the relative
proportion of metals in Middle Waterway sediments was compared to that
in (1) ASARCO slag, (2) a Pt. Defiance Shoreline station that showed visual
evidence of a high ASARCO slag content, (3) "Tuf-Kut" sandblasting material,
and (4) City Waterway sediments known to have a high content of sandblasting
grit (ASARCO slag and/or "Tuf-Kut"). Arsenic- to-heavy metals ratios in
each of these materials are shown in Table 7.5.1. The Middle Waterway
sediments had proportionately more copper and proportionately less arsenic
and zinc than either ASARCO slag or the Ruston-Pt. Defiance sediments
contaminated with ASARCO slag. In comparison to "Tuf-Kut," the Middle
Waterway sediments had proportionately much less copper. From these data,
it appears that either the ship repair firms along Middle Waterway are
using sandblasting products other than ASARCO slag or "Tuf-Kut," or some
material other than sandblasting grit is the major source of the metals
contamination observed.
Antifouling paints may be a potential source for these metals. A
wide variety of metals are used as toxicants 1n antifouling paints, including
copper, mercury, and tin. These and other metals have been found at elevated
concentrations 1n marine sediments adjacent to ship repair facilities (Young
et al. 1979). Although the data are Inadequate to draw definitive conclusions,
antifouling paints removed by sandblasting may be contributing to the metal
contamination observed 1n Middle Waterway sediments.
7.177
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Table 7.5.1
COMPARISON OF ARSENIC AND METAL RATIOS IN MIDDLE WATERWAY SEDIMENTS
Mouth of Middle Waterway (MD-13)
ASARCO slag3
Pt. Defiance shoreline (RS-24)
"Tuf-Kut" blasting sand'5
City Waterway off Martinac
Shipbuilding
(WDOE Station CS-5)
Contaminant Concentration (mg/kg) and Ratio
As
Zn
Cu
Hg
67
158
554
3.4
(1)
(2.4)
(8.3)
(0.051)
9,000
18,000
5,000
no data
(1)
(2)
(0.55)

700
1,620
385
0.41
(1)
(2.3)
(0.55)
(0.00059)
<0.8C
75
1,300-5,000
0.06
(1)
(93.8)
(1,600-6,250)
(0.75)
197
2,100
2,160
0.035
(1)
(10.7)
(U)
(0.00018)
aSource: State of Washington Discharge Permit Application, 1971, ASARCO
^Source: Norton and Johnson 1984.
cThe arsenic concentration of <0.8 mg/kg was supplied by the manufacturer of
"Tuf-Kut." In May 1980, the Washington Department of Industry, Division of
Industrial Safety and Health, analyzed the "Tuf-Kut" blasting sand at Peterson
Boats for arsenic and reported 20 mg/kg (0. Burt, Division of Industrial Safety
and Health pers. comm.).
7.178
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MIDDLE WATERWAY
7.5.4.4 Summary and Recommendations--
The gradient of metals contamination along the length of Middle Waterway
suggests that the source of copper and mercury is located near the waterway
mouth. The sediment core data indicate that this source is recent and
possibly ongoing. The only known discharge to Middle Waterway containing
heavy metals is at the head of the waterway (the MD-200 storm sewer outfall).
The ship repair facilities along the western shore of Middle Waterway (i.e.,
Cook's Marine Specialties, Foss Tugs, and Marine Industries Northwest)
appear to be the most probable source of the copper and mercury in the
waterway sediments. The use and/or removal of antifouling paints containing
copper and mercury may generate metals. Release of sandblasting grit,
while not the sole source of the metals, may also be a contributing factor.
A WDOE inspection of the ship repair facilities near the mouth of
Middle Waterway is recommended. This inspection should emphasize sandblasting
practices and the extent to which blasting grit and bottom paints may be
reaching the waterway. Further sampling of waterway sediments is recommended
to better define spatial gradients of contamination and to determine whether
one of the several ship repair firms is the major source of metals.
7.5.5 Middle Waterway: Summary and Recommendations
Of the six preliminary contaminants or contaminant groups designated
to be of concern in Middle Waterway, possible sources for three (pentacnloro-
phenol, copper, mercury) have been identified. It is possible that dichloro-
benzenes and PAH are entering the waterway via the storm sewer system or
possibly via one of the other discharges at the head of the waterway.
Ultimate sources within the drainage area could not be identified.
Five industries have been identified as possible sources based on
their potential use of products containing the contaminants of concern
and their potential discharge to areas of the waterway showing the highest
sediment contaminant concentrations. These industries include:
• Champion International (or its predecessor, St. Regis Paper
Company) - potential source of pentachlorophenol via the
storm sewer system (may account for high sediment concentrations
near the drain at the head of the waterway)
• Coast Craft - potential unconfirmed source of pentachlorophenol
(used as a wood preservative) by spillage or other unauthorized
discharge
• Cook's Marine Specialties, Foss Tug, and Marine Industries
Northwest - potential sources of copper and mercury by release
of antifouling paints, sandblasting material, or other products
used in ship repair
7.179
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MIDDLE WATERWAY
• Paxport Mills - potential source of metals and organic compounds
from a wood waste and ASARCO slag mixture used as fill in
a salmon enhancement area near the mouth of the waterway.
Hiere has been no documented discharge of these preliminary contaminants
of concern from any named facility to Middle Waterway. However, inspection
of all these facilities is recommended. Ihtil this inspection is completed
and sources of these contaminants can be better identified, no further
recommendations regarding source control can be made, nor can the effectiveness
of source control be evaluated. Specific recommendations for each preliminary
contaminant and contaminant group were discussed elsewhere in Section 7.5.
7.180
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CITY WATERWAY
7.6 CITY WATERWAY
7.6.1 Introduction
The body of water that is now City Waterway was originally bounded
by the bluffs of Old Tacoma and the western side of the Puyallup River
delta. The 1886 nautical charts of the area (Hart-Crowser and Associates
undated) show shallows and mudflats across much of this area. Settlement
of Tacoma began along the western bluffs overlooking the tideflats, and
as early as the 1860s, wharves were built along the bluffs to accommodate
ship traffic (Morgan and Morgan 1984). The wharves were used to store
coal, grain, and wood for shipment to other ports. The lumber milling
industry began to expand as port facilities increased. By 1873, the Northern
Pacific Railroad had reached Tacoma. The terminus of the railroad, complete
with dock facilities, was built on the west side of the waterway near what
is now Stadium Way. The railroad provided the impetus for industrial develop-
ment near the city and across the tideflats. Old photographs show the
western shore of the waterway bulwarked against erosion by 1890. The first
known dredging occurred in 1890 when the Tacoma Land Company deepened the
channel for vessel entry. By 1894, the City Waterway had reached its present
length and width. Wheeler-Osgood Waterway was formed prior to 1894 from
the old western channel of the Puyallup River.
Industries along the waterfront in the 1890s and early 1900s included
10 - 15 warehouses and dock storage facilities, at least seven lumber mills,
two foundries, several food processing and storage companies, and two electric
companies. Industries presently surrounding City Waterway are shown in
Figure 7.6.1. Harmon Furniture, Fick Foundry, Northern Fish Products (now
Ocean Fish), and Union Oil of California were present prior to 1920 (Ruckelsnaus
1985). Much of the western shore of the waterway is occupied by marinas
and storage facilities. North Pacific Plywood, located on the western
shore since at least 1960, recently moved to Graham, Washington. Harmon
Furniture, George Scofleld Company, two seafood processors, and a wholesale
produce distributor remain on the west side. Major reconstruction on the
west side of the waterway is occurring with the building of a new 15th
Street bridge across the waterway.
American Plating 1s located near the head of the waterway along Its
eastern shore. The firm has been present at this location (with other
names and owners) since about 1955. Marinas front the eastern shoreline
of the waterway as far north as 15th Street. Burlington Northern and Union
Pacific Railroad Yards and several large grocery warehousing facilities
are on the east side of D Street near the head of the waterway. Martinac
Shipbuilding, north of 15th Street, has been at this location since 1925.
Wheel er-Osgood Waterway 1s ringed by abandoned buildings, warehouses, and
several small industries with unknown operations. Hygrade Foods, Carsten's
Meat Packers prior to 1960, 1s situated east of Wheeler-Osgood Waterway.
Woodworth and Company, a construction firm present since the 1930s;
Fick Foundry, present as early as 1920; Globe Machine; Olympic Chemical;
and the 0 Street petroleum facilities with multiple owners (Mobil, Shell,
7.181
-------
Puget Sound Plywood
"D" Street Petrol turn Facilities
D" Street Petroleum Facilities (multiple owners
Coast Craft
F1ck Foundry
0lyi*>1c Chemical
Globe Machine
Totem Marina
Woodworth & Co.
MSA Saltwater Boats
Western F1sh
Old St. Regis Door Mill (closed)
Old Tacoma Light
Colonial Fruit ft
Produce
Martinac Shipbuilding
Chevron
Hygrsde Foods
Johnny's Seafoods
Scofield, Tru-M1x,
N. Pacific Plywood
(closed)
Tar Pits Site
(Multiple owners)
West Coast Grocery
Vacant
Marina Facilities
Pickering Industries
J.H. Galbreith Co.
Union Pacific I
Burlington Northern
Railroads
Harmon Furniture
(Tacoma Spur)
0 500 1000
FEET
American Plating
Figure 7.6.1
INDUSTRIES SURROUNDING CITY WATERWAY
7.182
-------
CITY WATERWAY
Union and Superior oil companies) are located north of Wheeler-Osgood Waterway,
along City Waterway. Portions of the D Street tank farms have been present
since the 1920s.
Dredging in City Waterway by the U.S. Army Corps of Engineers has
not occurred since 1948; however, there have been several dredging activities
by private companies. A summary of recent dredging projects in City Waterway
is presented in Table 7.6.1. The Corps dredged the waterway every 3 to
12 yr between 1905 and 1948 (Johnston 1981). Since that time, minor revisions
in shore configuration have been conducted mainly to install docks and
marina facilities. U.S. Army Corps of Engineers permit records indicate
construction of bulkhead and docks for marina facilities for MSA Salt Water
Boats on the west side of the waterway south of 15th Street, Pickering
Industries, and the Picks Cove restaurant area next to Pickering Industries.
None of these minor projects was in an area sampled by Tetra Tech or WDOE
during these Superfund investigations.
Major discharges into City Waterway, shown 1n Figure 7.6.2, include
the locations of major storm drains serving the waterway and the industrial
discharges permitted under the NPDES permit program. All NPDES-permitted
discharges to City Waterway are classed as minor Industrial discharges.
NPDES permits for these industries typically include permit limits for
flow, pH, temperature, total oil and grease, and BOD. They do not include
discharge limits or monitoring requirements for U.S. EPA priority pollutants.
Storm drains entering City Waterway have served the area since the
turn of the century. Until 1979, six major combined drains serving 11,000
ac and a population of 60,000 or more discharged to City Waterway. These
drains included the 11th, 15th, and 21st Street drains (CI-235, CI-230,
CI-234, respectively); the Nalley Valley drain (CN-237); the south Tacoma
drain (CS-237); and the drain at the head of Wheeler-Osgood Waterway (CW-254).
Discharge of sanitary sewage through these drains was substantially decreased
in 1969 by efforts to separate the storm and sanitary sewers in the city
of Tacoma. Intermittent discharge of sewage through some of these drains
continued until 1979. Presently, the discharge from these drains to the
waterway consists of urban stormwater runoff. The Nalley Valley and south
Tacoma drains, at the head of the waterway, have the largest flows and
serve a major portion of the urban Tacoma area. Total suspended solids
(TSS) 1n these two storm drains are as high as 320 mg/L during storm events
(Johnson and Norton 1984c). Although 1t has a smaller discharge, the 15th
Street drain may carry suspended solids concentrations of similar magnitude.
The drain at the head of Wheeler-Osgood Waterway and the 11th and 21st
Street drains serve much smaller areas than the other drains, have much
smaller flows, and generally have lower TSS values.
7.6.2 Contaminants of Concern
Locations of sediment chemistry stations in City Waterway, including
those sampled as part of the Superfund Investigation and all historical
sampling sites are shown in Figure 7.6.3. City Waterway has been divided
into three segments: upper City Waterway to approximately 3,800 ft from
7.183
-------
TABLE 7.6.1. SUMMARY OF DREDGING PROJECTS, CITY WATERWAY
Year
Permitee
Quantity
(yd3)
Comments/Status®
1975
City of Tacoma
4,750
Completed in 1977
1977
Johnny's Dock Restaurant
8,464
Completed
1977
Pickering Industries
2,100
Completed
1978
Morris and Sons
2,500
Completed
(per file note)
1979
M. W. Perrow
4,820
Completed
1981
S. Jones
3,600
Status unkown
1982
J. E. Meaker
364

1983
Superior Oil Company
5,000

a Except where noted, all project status was verified by Duane Kama, U.S. EPA.
Reference: U.S. Army Corps of Engineers dredging permits, as compiled
by M. Ruckelshaus, WDOE.
7.184
-------
CI-059
CI-zlz
CI-060
CI-221
CI-222
CI-223
CI-224
C1-22S Uth St. Or* In
Union Oil Co. HPDES MA000072B r, ,17
Mobil Oil Corp. NPDES MA0003387 .t."
Shell Oil Co^ NPDES WA0001210 CI*"6
CI-214
CI-213
CI-211
CI-210
Fick Foundry NPDES WA0037B51
-209
CI-208
CI-226
C1-227 Western F1sh t Oyster Co:
NPDES WA0022853 CN228
CI-229
CI-230 15th St. Drain
CI-231—1
CI-232 George Scofleld Co
NPDES WA0003298
CI-233
CI-703 Drain at Hanm Furniture
CI-234 21st St. Drain -»
Atlas Foundry NPDES UA0022918
CI-219
CI-218
CI-215
CI-207
CI-206
£
CI-249
CI-244
JZ

-CM-2S4 Mteeler-Osgood Drain
-CH-253
CI-248
CI-247
CI-246
CI-245 Drain from Railroad Yards
CI-243 Drain from Railroad Yards
-CI-242 CI_m
CI-219
-CI-238
CN-237 Nalley Valley Drain gS-237 south Tacom Drain
METERS
Figure 7.6.2
STORMDRAIN LOCATIONS AND NPDES PERMITTED
DISCHARGE LOCATIONS IN CITY WATERWAY
7.185
-------
+ WDOE, 1984
0 WDOE, Historical
A EPA
~ Tetra Tech
X Other Agencies
North
Sediment Core
Sediment Core CI-61
CI-63
Sediment Cor
CI-62
Sediment Core
CI-60
500
1000
Figure 7.6.3
SURFICIAL SEDIMENT STATIONS AND SEDIMENT CORE LOCATIONS
FROM ALL STUDIES IN CITY WATERWAY
-------
CITY WATERWAY
the mouth (Segment 1); Wheeler-Osgood Waterway (Segment 2); and lower City
Waterway to the mouth (Segment 3). Eight chemicals or groups of chemicals
plus organic enrichment have been named as contaminants of concern in one
or more segments of City Waterway. These contaminants and their respective
areas of concern include:
Organic Compounds Metals
Organic enrichment (Segments 1, 2) Copper (Segments 1 and 3)
Aromatic hydrocarbons (Segments 1, 2, and 3) Lead (Segments 1 and 3)
Dibenzofuran (Segments 1 and 3) Zinc (Segment 1)
Dichlorobenzenes (Segments 1, 2, and 3)
4-Methylphenol (Segments 1, 2, and 3)
PCBs (Segments 1 and 3)
Dibenzofuran is listed as of preliminary concern in Segment 1 and
3 and source evaluations were conducted for this compound. It was later
determined that concentrations of dibenzofuran did not exceed AET at any
station in City Waterway. Concentrations of other chemicals listed above
as of preliminary concern in Segments 1 and 2 did exceed AET for at least
one station in those segnents. Aromatic hydrocarbons, PCBs, and zinc concentra-
tions exceeded AET in Segment 3, but concentrations of the other preliminary
contaminants of concern in Segment 3 did not. PCBs were also of concern
in this waterway because of significant bioaccumulation in English sole
muscle tissue.
Other contaminants for which concentrations were ultimately determined
to exceed AET (see Table 6.14 in Section 6) but were not subjected to source
evaluations included:
Substance Station Where AET (DW) Exceeded
2-Methylphenol CI-12, CI-15
Phenol CI-02, CI-11, CI-20
Benzyl alcohol CI-11
N-nitrosodiphenylamine CI-01, CI-02, CI-16, CI-18
Phthalate esters CI-12, CI-13
Cadmium CI-02, CI-12, CI-13, CI-14, CI-15,
CI-18
Mercury CI-01, CI-03, CI-11, CI-13, CI-18
Nickel CI-11 and intertidal sediments
Aniline was detected at a single station (CI-01) at the head of City Waterway.
AET could not be determined for this canpound. Concentrations of two tentative-
ly identified compounds were also determined to exceed AET 1n City Waterway
[I.e., blphenyl 1n Segment 2 and 3, and dlbenzothlophene 1n Segment 3).
These latter substances likely share conmon sources with PAH.
Mercury was not of preliminary concern, but source evaluations are
needed because 1t was later determined to be a Priority 1 chemical in City
Waterway (i.e., mercury was present above AET and its concentration gradient
7.187
-------
CITY WATERWAY
covaried with changes in polychaete abundances; see Section 4.2.3.3).
A brief summary of its distribution is presented here. Loading data are
presented in the report on potential remedial technologies for the Commencement
Bay nearshore/ tideflats remedial investigation (Tetra Tech 1985). Highest
concentrations of mercury occurred at Stations CI-13 (1.1 ug/kg dry weight)
and C1-18 (0.96 ug/kg dry weight). Even higher concentrations were found
at depth in mid-channel cores from Stations C1-60, CI-61, and CI-63 (maximum
2.7, 1.6, and 2.5 ug/kg dry weight, respectively). The spatial pattern
observed for mercury concentrations did not correlate well with that of
other metals believed to derive primarily from drains at the head of City
Waterway. Ninety-three percent of the known loading of mercury derives
from the 15th Street drain (CI-230). The other substances for which source
evaluations were not conducted are not discussed further.
The distribution of each preliminary contaminant of concern in the
surficial sediments of City Waterway using data from Superfund studies
and all historical information is presented in Figure 7.6.4. This figure
is presented to show the areas of the waterway that are the most contaminated
and to allow visual parallels to be drawn among the distributions of the
contaminants. (Contaminants with similar distributions may have common
sources.) The fine lines indicate areas where the concentrations of the
contaminant exceeded the 80th percentile of that contaminant's concentrations
in all stations sampled as part of this Superfund study. The heavy lines
indicate areas that exceeded the 90th percentile of the concentrations
in these stations. This figure illustrates areas of elevated concentrations
for each contaminant. These areas may not coincide with those designated
to be of concern for each contaminant, since the designation of an area
of concern incorporates biological as well as chemical data.
Three trends are readily apparent from Figure 7.6.4:
1. A greater number of the contaminants of concern had elevated
concentrations 1n sediments at the head of the waterway
than near the mouth.
2. Copper, lead, zinc, and total organic carbon had similar
concentration gradients, suggesting a common source for
these four contaminants.
3. Several contaminants of concern showed elevated concentrations
in Wheeler-Osgood Waterway, yet had much lower concentrations
in nearby City Waterway sediments. This suggests the presence
of sources in Wheeler-Osgood Waterway.
Average mass flux estimates were calculated for HPAH, LPAH, copper,
lead, and zinc to enable a comparison of mass loadings of these contaminants
relative to their sediment concentrations 1n City Waterway. Insufficient
source data were available to calculate mass flux estimates for the other
priority contaminants. The mass flux estimates were evaluated using average
concentrations of the contaminants 1n sediments from all present and historical
stations according to the procedures and criteria outlined in Section 2.12.3.2.
7.188
-------
Total Organic Carbon j
Low Molecular Wt. PAH
High Molecular Wt. PAH
Dibenzofuran
1,2-dibhlorobenzene
1,4-dichlorobenzene
4-methyl phenol
PCB
Copper
Zinc
Lead
Contaminant Concentrations
Exceed 80th Percentile
Contaminant Concentrations
Exceed 90th Percentile
o:
o>;
tn ;
-------
CITY WATERWAY
All of the source-derived mass fluxes were within an order of magnitude
of the concentration-derived mass fluxes with the exception of HPAH. Therefore,
according to the uncertainty criteria for this analysis, no data gaps were
indicated in accounting for major sources of LPAH, copper, lead, or zinc.
The source-derived mass flux for HPAH was less than 1 piercent of the concentra-
tion-derived mass flux. A data gap in the identification of HPAH sources
was indicated.
In the following sections, each contaminant of concern is individually
addressed. Its spatial distribution within the waterway sediments is discussed,
contaminant loadings from known sources are presented, and all known or
potential sources are evaluated. Two dimensional plots of contaminant
concentrations, which have been used for other waterways to display spatial
distributions, are not presented for City Waterway. Instead, all concentration
plots are presented as changes in concentration with distance from the
mouth of the waterway because of the linear arrangement of almost all stations.
The location of critical stations is described in text when the spatial
pattern was unclear from these plots.
7.6.3 Organic Enrichment
Sediment organic enrichment, measured as total organic carbon (TOC),
represents a measurement of total organic content regardless of compound
or oxidation state (American Public Health Association et al. 1981). It
includes the organic carbon from detritus carried in stormwater runoff
(e.g., leaves and bark), domestic and industrial wastewater organic chemicals,
oils and grease, and all other organic contaminants entering the waterway.
7.6.3.1 Spatial Distribution--
Organic enrichment and anoxic sediments are of concern in Segments
1 and 2 of City Waterway. Waterway sediments (especially 1n Wheeler-Osgood
Waterway) contained some of the highest levels of organic carbon seen anywhere
in the tideflats area. In surficial sediments, concentrations of organic
carbon decreased from the head of the waterway to the mouth (Figure 7.6.5).
In Segment 2 (Wheeler-Osgood Waterway), organic carbon was measured at
10.9 - 18.0 percent. This pattern of organic enrichment indicates at least
one source of organic carbon at the head of the waterway and another in
the Wheeler-Osgood Waterway.
Organic carbon concentrations 1n sediment cores collected in City
Waterway are shown 1n Figure 7.6.6. At the head of the waterway (Station
CI-60, G05), organic carbon concentrations decreased only slightly with
depth down to 4.3 ft (1.3 m) 1n the sediment column, Indicating a relatively
constant rate of accumulation of organic carbon over time. Core samples
from Wheeler-Osgood Waterway (CI-62, G01, B02) and from City Waterway near
the mouth of Wheeler-Osgood Waterway (CI-63, B01) did not penetrate as
deeply as other City Waterway cores. However, there was little evidence
of change 1n the rate of organic Input to the depth sampled (1.3 ft; 0.4 m).
Core CI-61, G01, collected In the lower third of the waterway (about 3,000
ft from the mouth) showed a fivefold increase 1n organic carbon beneath
7.190
-------
Segment:
18
17
16 -
1 5 -
1 4 -
1 3 -
12 -
1 1 -
10 -
9 -
8
7 -
6 -
5
4
3
2 -
1 -
0
1 2
i9-
_©
~
° • rn
O D
Benthlc effects
and Toxicity
AET
2 4 6
(Thousands)
Ft. from mouth of waterway
8
~ T*tr« Itch ]nv*st1git1on - Quint U» ted v»lue
0 Other Investigations • Quintit»ted vtlue
Figure 7.6.5
SURFICIAL SEDIMENT CONCENTRATIONS OF
TOTAL ORGANIC CARBON IN CITY WATERWAY
7.191
-------
1.
2 •
3 *
4 *
5 *
6 *
7 •
8 "
9 "
0 ¦
1 '
2 •
3 *
4 -
5 *
' ' ' ' '
1%
1_
..iii...
U-CI-63.
^ B01 :
i
i :
10%
j±
100f,
CI-61
G01
1
L,
CI-60
G05
rCI-62—
bo 2 :
i
i...
CI-62
G01
¦Benthic effects
and toxicity
AET
Figure 7.6.6
PERCENTAGE OF TOTAL ORGANIC CARBON
WITH DEPTH IN SEDIMENTS OF CITY WATERWAY
(For station locations refer to Figure 7.6.3)
7.192
-------
CITY WATERWAY
1.6 ft (0.5 m) to concentrations corresponding to those observed in other
City Waterway cores. This increase suggested that current organic carbon
discharges to the lower waterway are considerably less than historical
discharges. Alternatively, substantial dilution of the organically enriched
material accumulating elsewhere in City Waterway may now occur in the lower
City Waterway where it may not have in the past.
7.6.3.2 Loading Estimates--
The chemical oxygen demand (COD) of discharges to City Waterway provides
the only means available to estimate the relative contribution of these
discharges to the total organic carbon content of waterway sediments.
COD can be empirically related to the BOD, organic carbon, or organic matter
content of the source (American Public Health Association et al. 1981).
Johnson and Norton (1984c) summarized all COD data available in City Waterway
storm drains (Table 7.6.2). The south Tacoma drain (CS-237) and the Wheeler-
Osgood drain (CW-254) each contributed 35 - 37 percent of the quantified
COD loading to the City Waterway/Wheeler-Osgood Waterway system. The COD
data for the Wheeler-Osgood drain are highly suspect due to interference
from the presence of saltwater.
The only NPDES-permitted discharger to City Waterway whose permit
specifically addresses BOD or COD is Hygrade Foods (Permit WA9002078-8,
expired 7/8/80). This firm discharges runoff and noncontact cooling water
to the Wheeler-Osgood Waterway. Although process effluents are not to
be discharged to the waterway, this has reportedly occurred as a result
of unidentified cross-connections between the cooling water and process
sewer (WDOE Hygrade files). Other industries are permitted to discharge
oil and grease, which would contribute to TOC loading. They include Fick
Foundry (Permit WA0037851), Shell Oil (WA0001210), Union Oil (WA0000728),
Atlas Foundry (WA0022918), and Mobil 011 (WA0003387). Western Fish and
Oyster Company has an NPDES permit (WA0022853) to discharge screened process
wastewater to City Waterway. The firm 1s not required to monitor for BOD,
but 1t is probably not a major source of organic carbon based on the low
discharge volume.
7.6.3.3 Source Identification--
From the turn of the century to the 1970s, City Waterway was one of
the main recipients of wastes from combined sewer outfalls in the Tacoma
area. As of 1950, there were six untreated sewage outfalls entering the
waterway, serving an area of about 11,000 ac and more than 60,000 people.
In addition, untreated industrial effluent entered via these sewers (Orlob
et al. 1950). Locations of the six outfalls Included two outfalls at the
head of the waterway (now called the Nalley Valley and south Tacoma drains);
the 11th Street, 15th Street, and 21st Street drains; and a drain at the
head of Wheeler-Osgood Waterway. In addition to domestic sewage, these
sewers probably carried wastes from Nalley's Foods, Model Pickle Company,
Fassett and Company, Tacoma Vegetable Oils, Copes Poultry, and several
dairies. The total estimated BOD loading from these Industries alone in
1950 was greater than 1,000 lb/day (Jones 1951; based on a population-equivalent
7.193
-------
Table 7.6.2
COD: SUMMARY OF LOADINGS FROM DISCHARGES TO CITY WATERWAY
Drain #
Drain Name
Flow (HGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(I of Observations)
Loading (lbs/day)
(Avg. and Range)
CW-254
Wheeler-Osgood Drain,
30-Inch Steel Pipe
0.29
(0.13-0.63)
(n-4)
7/28/81-3/29/82
330.000
(170,000-490.000)
(n-2)
800
(410-1,200)
CS-237
South Tacoma Drain
4.8
2.S8-10.98
(n-4)
7/28/81-2/16/81
19,000
(4,000-33.000)
(n-2)
760
(160-1,300)
CN-237
Nalley Valley Drain
3.6
1.2-10.66
(n-8)
7/28/81-2/16/82
11,000
(4.000-18.000)
(n-2)
330
(120-540)
CI-230
15th Street Drain
48-1nch Concrete Pipe
0.17
(0.14-0.22)
(n»3)
4/28/82
190,000
(n-i)
270

Note: The data for the Wheeler Osgood drain (CH254) are highly suspect due to Interference from the presence of
saltwater.
7.194
-------
CITY WATERWAY
of greater than 5,000). This estimate probably did not reflect the total
discharge via sewers from food processors in this service area, since Jones
(1951) did not specify outfall locations for many industries except to
comment that they discharge to "City Sewer." The size of the area dis-
charging to City Waterway makes it probable that a number of additional
food processors ultimately discharged to the waterway via the sewer system.
As a consequence of the volume and nature of the wastes historically
discharged to City Waterway, the environmental quality of the waterway
had badly deteriorated by the mid-1900s. Orlob et al. (1950) described
the condition of the waterway at the time as follows:
The condition of the waterway as a result of the sewage discharge
from these sewers and the added industrial waste effluents, partic-
ularly that of a large meat packing plant, has long been a source
of embarrassment to many of Tacoma's residents and has given
rise to numerous complaints in recent years. Since the only
water entering the waterway is either in the form of sewage or
industrial waste and there is little exchange of water due to
tidal action, the area so affected amounts to little more than
a septic pool, the bottom of which is covered with organic deposits
devoid of any life and in which fish either could not or do not
choose to live.
Improvement in the environmental quality of City Waterway occurred
in the late 1960s when efforts were made to reroute the sanitary and industrial
wastes from City Waterway to the Central Treatment Plant (Kennedy Engineers
1969; O'Dell, C., personal communication). Because of cross-connections
between the sanitary and storm sewers, sewage contamination of the Nalley
Valley drain continued until 1979, when an interceptor was Installed at
23rd and B Streets. Tacoma Sewer Utilities believes that installation
of this interceptor has corrected the problem of sewage in the discharge
of the Nalley Valley drain (O'Dell, C., personal communication). In 1982,
the WDOE found that fecal coliform bacteria concentrations in the discharge
far exceeded those of any other drain to the waterway (1,800 - 14,000/100
mL; Johnson and Norton 1984b). These fecal coliform bacteria may reflect
contamination by domestic sewage or simply domestic animal (e.g., pet)
waste in stormwater runoff.
Several fish processors (Northern F1sh Products, Marush Fish and Oyster
Company, and possibly National Fish and Oyster Company) along Dock Street
dumped wastes directly into City Waterway (Jones 1951). By 1979, Western
Fish and Oyster Company, at 1137 Dock Street, was the only company permitted
to discharge screened process water and washwater directly to the waterway
(NPDES Permit WA0022853).
A major historical source of total organic carbon to Wheeler-Osgood
Waterway was Carsten's Packing Company. A slaughtering/packing plant,
the firm's only treatment of process wastes consisted of grease skimmers,
and they were Inadequate. The estimated BOD loading from this discharge
alone was 8,800 lb/day based on a population equivalent of 44,000 (Jones
7.195
-------
CITY WATERWAY
1951). The facilities were leased to Hygrade Foods about 1955 and bought
by Hygrade about 1960. Discharge of all process wastes to Wheeler-Osgood
Waterway continued until 1970, when the process wastes were rerouted to
the Tacoma Central Sewage Treatment Plant (O'Dell, C., personal communi-
cation). As a result of unidentified cross-connections, some process wastes
continued to be discharged to Wheel er-Osgood Waterway along with cooling
water and runoff through the mid-1970s. At the present time, the firm
has an NPDES permit for discharge of runoff and noncontact cooling water
to Wheeler-Osgood Waterway.
7.6.3.4 Summary and Reconmendations-
Six discharges are known to have been major sources of organic carbon
to City and Wheeler-Osgood Waterways. Only two or three (Nalley Valley
and/or south Tacoma, Wheeler-Osgood) are implicated as major sources by
the spatial pattern of organic enrichment in surficlal sediments. Source
identification efforts have been directed at these discharges. Both the
Nalley Valley and south Tacoma drains discharged untreated sewage to the
head of City Waterway through 1969. Significant quantities of sewage were
discharged from the Nalley Valley drain until 1979. One or both of these
drains is responsible for the increase 1n organic enrichment in surficial
sediments from the mouth to the head of City Waterway.
The Wheeler-Osgood drain is believed to be a major source of the organic
enrichment noted in the surficial sediments of Wheeler-Osgood Waterway.
The Wheeler-Osgood drain historically discharged untreated sewage and process
wastes from Carsten's Packing Company and Hygrade Foods. Discharge of
organic material from this drain should have been substantially reduced
in 1969-1970 with the diversion of process wastes and sewage to the Tacoma
Central Sewage Treatment Plant. However, some discharge of process wastes
continued until the mid-1970s because of unidentified cross-connections
between process and storm sewers.
Although the drains noted above had been major sources of organic
material, it is difficult to determine the extent to which they serve as
ongoing sources of organic material to City and Wheeler-Osgood Waterways.
Discharge of significant amounts of organic material from these drains
should have ceased in the 1970s, yet organic enrichment of 9 - 18 percent
total organic carbon was apparent in surficial sediments. Similar elevations
in organic carbon concentrations were not apparent at the outfalls of other
storm drains 1n the tldeflats area. In addition, the sediment cores at
the head of City Waterway and in Wheeler-Osgood Waterway showed no evidence
of any reduction in the rate of organic carbon Input over time, although
a decrease was expected given the discharge history of the major drains.
Decaying wood and vegetation 1n the stagnated Wheeler-Osgood Waterway may
contribute to the substantial organic enrichment observed.
Sediment accumulation rates 1n City and Wheeler-Osgood Waterways could
be used to evaluate 1) if possible slow sedimentation 1n these areas has
resulted in minimal burial of historically contaminated sediments, or 2)
1f relatively rapid sedimentation has occurred indicating an ongoing source
7.196
-------
CITY WATERWAY
to account for continued high levels of organic enrichment. No site-specific
estimates of these rates have been made for these waterways. Based on
sampling throughout Puget Sound (Riley 1981; Crecelius 1983; Carpenter
in press), 1 cm/yr may be used as a crude approximation of a typical surface
sedimentation rate. It is recognized that sediment accumulation rates
in City and Wheeler-Osgood Waterways may be very different from sediment
accumulation rates in Puget Sound, and may differ even between the two
areas. Assuming an accretion rate of 1 cm/yr, approximately 6 cm of sediment
may have been deposited since the last known major discharge of organic
material in 1979. In any event, if deposition rates in City Waterway are
comparable to or greater than those in other areas of Puget Sound, adequate
time should have elapsed to bury organic-rich sediments beneath sediments
of lower organic content provided the major input of organic carbon actually
ceased in or before 1979 and no major disturbances of the sediments has
occurred.
The fact that organic enrichment is observed in surficial sediments
upper 2 cm) suggests two possibilities: (1) burial of enriched sediments
n City Waterway, or particularly Wheel er-Osgood Waterway, is slower than
predicted or (2) significant discharge of organic carbon from the Nalley
Valley or south Tacoma drains to City Waterway has continued beyond 1979
and a current source of organic carbon (possibly natural) exists in Vlheeler-
Osgood Waterway. Available data are not adequate to determine conclusively
which of these two explanations 1s correct. The data Indicate that discharges
of organic material from the Nalley Valley or south Tacoma drains persist.
This conclusion is supported by the fact that each of the two major storm
drains had a flow of about 4 MGD and a total suspended solids loading of
about 7,000 lb/day (Table 7.6.2, Johnson and Norton 1984c). Moreover,
as recently as 1982, the Nalley Valley drain was found to have fecal coliform
bacteria concentrations up to 15 times greater than those in any other
storm drain discharging to City Waterway.
Investigations should be undertaken to determine the origin of the
organic carbon 1n the Nalley Valley and south Tacoma drains. Investigations
into organic carbon sources to these drains should include analyses for
chemical/biological indicators of sewage contamination (e.g., coprostanol,
fecal conform bacteria). The Wheel er-Osgood drain should be investigated
as a source of organic material. Natural sources of organic enrichment
in Wheeler-Osgood should also be considered.
7.6.4 Aromatic Hydrocarbons and Dlbenzofuran
7.6.4.1 Spatial Distr1but1on--
HPAH, LPAH, and dlbenzofuran were Identified as preliminary contaminants
of concern 1n City Waterway. Concentrations of HPAH and LPAH exceeded
AET 1n some sediments from several areas of the waterway. LPAH concentrations
ranged from 500 to 21,000 ug/kg dry weight In City Waterway; most concentrations
were less than 5,000 ug/kg dry weight (Figure 7.6.7). Concentrations of
HPAH ranged from 4,700 to 82,000 ug/kg dry weight; most concentrations
were less than 20,000 ug/kg dry weight (Figure 7.6.8).
7.197
-------
£
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Segment:
22
1 2
21 -
20 -
19 -
18
17
16
15
14
13
12
1 1
10 -
9 -
8 -
7 -
6 -
5 -
4 -
3 -
2 -
1 -
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11£"
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(Thousands)
Ft. from mouth of waterway
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250
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150
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Benthlc effects
AET
not exceeded
Toxicity
AET
(B)
(Thousands)
Ft. from mouth of waterway
~ Tttri Tech Investigation • QutntHittd Vtlut
0 Other Inmtlgettoni - QuintUittd Vtlu*
A Tetr* Tech Investlgetlon • lest Thin Vllue
V Other Investigations - Less Thtn Value
* Tetra Tech Investigation • Undetected Value
X Other Investigation - Undetected Value
Figure 7.6.7
SURFICIAL SEDIMENT CONCENTRATIONS OF LPAH
IN CITY WATERWAY, (A) DRY WEIGHT BASIS, (B) NORMALIZED
TO TOTAL ORGANIC CARBON
7.198
-------
Segment:
90
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Effects
AET
Toxicity
AET
(Thousands)
Ft. from mouth of woterwoy
Segment:
8
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0.9 -
0.8 -
0.7 -
0.6 -
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1 2
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fi
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2 4 6
(Thousands)
Ft. from mouth of woterwoy
Benthlc effects
AET
not exceeded
Toxicity
AET
(B)
e
O T»tr» T«cfi - 0ui»t1t«t«d V«lu«
0 Dltwr lnvf >t tgiUoni - QutntiUtt) Vtluf
A T»tr» Itch Investigation - Ltis TMn Vtluc
V Otlwr Inmttgitlons - UK Thin Vtluc
* Tftrt T«ch Jnv«»t1git1on • Undctcetttf Vilut
X Other InMStigttloft * Undetected ftlu*
Figure 7.6.8
SURFICIAL SEDIMENT CONCENTRATIONS OF HPAH
IN CITY WATERWAY, (A) DRY WEIGHT BASIS, (B) NORMALIZED
TO TOTAL ORGANIC CARBON
7.199
-------
CITY WATERWAY
Sediments from a single station in the middle of Wheeler-Osgood Waterway
(sampled by the U.S. EPA; Swartz et al. 1982) contained LPAH and HPAH at
concentrations (dry weight) several times greater than those at any other
site sampled within the waterway. A second sample collected by U.S. EPA
near the head of Wheeler-Osgood Waterway (see Figure 7.6.3) was approximately
one tenth as contaminated. However, LPAH concentrations normalized to
organic carbon were three times higher near the head than at any of the
stations in the middle of Wheel er-Osgood Waterway (Figure 7.6.7b). These
data suggest a source of LPAH near the head of the waterway to account
for the highest proportion of LPAH to total organic carbon, but much greater
accumulation of contaminated, organic-rich sediments in portions of the
middle of the waterway. There was no obvious gradient in HPAH concentrations
after normalization to organic carbon.
In the main channel of City Waterway, LPAH and HPAH concentrations
normalized to organic carbon were approximately five times higher in sediments
near the mouth of the waterway than the average in sediments elsewhere
(Figures 7.6.7 and 7.6.8). These data suggest a source of PAH in addition
to transport of contaminated organic material from drains at the head of
City Waterway. The PAH source appears to be localized near the mouth of
the waterway. Because the highest PAH concentrations (when normalized
to organic carbon) were found in mid-channel sediments rather than 1n nearshore
sediments (i.e., the eastern shoreline sampled by WDOE), there is little
evidence of a direct link to a PAH source on the adjacent shoreline.
No other sites in City Waterway had significantly elevated sediment
concentrations of LPAH or HPAH. With the exception of the waterway mouth,
PAH concentrations throughout the main channel of City Waterway were relatively
uniform, with no evidence to suggest proximity to a dominant PAH source.
Spatial and depth trends of dibenzofuran concentrations resembled
those of LPAH in City Waterway on both a dry-weight and organic carbon-
normalized basis. Surface sediment concentrations ranged from 30 to 450
ug/kg dry weight (340 to 14,000 ug/kg T0C). This correlation with LPAH
was found throughout the tideflats.
The vertical patterns of sediment contamination by LPAH were similar
throughout the waterway, with somewhat elevated concentrations at depth
(Figure 7.6.9). PAH concentrations 1n both composited intervals of the
core from Wheeler-Osgood Waterway were higher than that observed in 0-2
cm sediments from the same area. A subsurface maximum 1n PAH concentrations
has been observed in other sediment cores 1n central Puget Sound and 1s
likely related to greater PAH discharges in past years (Crecelius and Bloom
in review; Barrlck and Prahl in review). The cores at the head and near
the mouth of the waterway (Stations CI-60 and CI-61) showed similar LPAH
profiles. The vertical pattern of sediment contamination by HPAH (Figure
7.6.10) was similar to that of LPAH, except for CI-61. The lowest horizon
of this core had proportionately more LPAH than HPAH in comparison with
other horizons within this core.
7.200
-------
1000
Concentration (ug/Kg-dry weight)
10,000
100,000
Benthic effects
and toxicity
AET
CI-61
CI-60 —
G05
Figure 7.6.9
CONCENTRATION OF TOTAL LPAH ON A DRY WEIGHT BASIS
WITH DEPTH IN SEDIMENTS OF CITY WATERWAY
(For station locations refer to Figure 7.63)
7.201
-------
Concentration (yg/Kg-dry weight)
1000
10,000
I i I l I I
100,000
CI-60—*-
GO 5
Toxicity ¦
AET
CI-63"
B01
CI-62"
B02
•—CI-61
;-!! ! 601
rti
!!
!'
i
Bent hie
Effects
AET j J
I.
Figure 7.6.10
CONCENTRATION OF TOTAL HPAH ON A DRY WEIGHT BASIS
WITH DEPTH IN THE SEDIMENTS IN CITY WATERWAY
(For station locations refer to Figure 7.63)
7.202
-------
CITY WATERWAY
Relative abundance of HPAH to LPAH in sediment cores was compared
to discriminate discharges by various sources over time. The results are
shown in Table 7.6.3. Except for sediment core CI-61 (Segment 3), the
ratios of HPAH to LPAH were similar in magnitude to those in surficial
sediments measured in the Tetra Tech survey. The aromatic hydrocarbons
in the subsurface sediments at CI-61 showed a much higher abundance of
HPAH relative to LPAH at this site, potentially indicating a historical
combustion source of HPAH or dumping of combustion products in this vicinity.
7.6.4.2 Loading Estimates-
Aromatic hydrocarbons have seldom been detected in stonm drain discharges
around City Waterway with detection limits ranging from 0.1 to 1 ug/1.
None of the storm drains with detectable levels of LPAH and HPAH showed
consistent contamination. Naphthalene, anthracene, and phenanthrene of
the LPAH, and pyrene, fluoranthene, and benzo(g,h,i)perylene of the HPAH
were the only compounds measured in any drain (Tables 7.6.4 and 7.6.5).
Based solely on the limited data available, the 15th Street drain appears
to be the largest source of PAH among the discharges considered. Only
the Nalley Valley drain (CN-237) has been analyzed for dibenzofuran. None
was detected (detection limits were 0.1 and 0.3 ug/L).
7.6.4.3 Source Identification--
The surficial sediment chemistry data suggest a source of both LPAH
and HPAH near the mouth of City Waterway. The sediment core data from
the mouth of the waterway indicate that sources of PAH have historically
had a greater proportion of HPAH relative to LPAH than do ongoing sources.
Three potential historical sources of these HPAH have been identified:
(1) marina fires, (2) Fick Foundry, and (3) Woodworth and Company. Data
were inadequate to demonstrate with certainty that these were the maior
sources of contamination. In addition, PAH contamination in surficial
sediments suggests an ongoing source and the three identified above are
all historical.
Johnson and Norton (1984b) have suggested that fires may be responsible
for elevated HPAH concentrations 1n sediments near the mouth of City Waterway.
There were two major dock fires near the mouth of City Waterway in the
1970s (Mork, S., personal communication). There have been no fires 1n
the area 1n at least the past 6 yr.
Fick Foundry 1s located near the mouth of City Waterway along the
eastern shore. At present, the firm uses natural gas to fire its furnaces.
However, 1t was not determined during these investigations if this has
always been the case. Past use of coal or heavy fuel oil could have been
a source of HPAH.
Woodworth and Company own property on the east shore of City Waterway
at the foot of the 11th Street bridge. Prior to 1977-1978, the firm operated
an asphalt plant with a wet scrubbing system to reduce atmospheric emissions.
Discharge from the wet scrubbing system was routed to a settling pond and
7.203
-------
Table 7.6.3
RATIO OF HIGH MOLECULAR WEIGHT PAH TO LOW MOLECULAR WEIGHT PAH
WITH DEPTH IN THE SEDIMENTS OF CITY WATERWAY
Station Location Horizon Ratio
CI-60 Segment 1 - Head of HI 3.4
(G05) the waterway, approx. H2 2.3
7,600 ft from mouth H3 2.7
H4 2.0
H5 1.3
CI-63 Segment 1 - Approx. HI 2.8
(B01) 4,600 ft from mouth H2 3.1
H3 2.6
CI-62 Segment 2 - HI 2.3
(B02) Wheeler-Osgood H2 2.3
CI-62 Segment 2 - HI 1.9
(G01) Wheeler-Osgood H2 1.4
CI-61 Segment 3 - Approx. HI 9.2
(GOD 3,500 ft from mouth H2 11
H3 8.7
H4 2.4
7.204
-------
Table 7.6.4
LOW MOLECULAR WEIGHT PAH: SUMMARY OF LOADINGS
FROM DISCHARGES TO THE CITY WATERWAY
Drain #
Drain Nmm
Flow (MGD)
(Avg and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (tig/1)
(Avg and Range)
(I of Observations)
Loading
I1bs/day)
(Avg and Range)
Compounds
Detected
Cl-230
I5th St. Storndraln,
48* Concrete Pipe
0.17
CO.14-0.22)
t»*3)
4/28/82,9/7/83
L 31
(18-60)
(n=2)
L 0.44
(0.0026-0.085)
Naphthalene,
Phenanthrene
OI-237
Nalley Valley Drain
3.6
(1.2-10.66)
(ft*8)
7/28/81,no date
L 5.2
(0.4-10)
(n*2)
L 0.16
(0.012-0.30)
Naphthalene,
Anthracene
CS-237
South Tkom Drain
4.8
(2.58-10.98)
{»»•«)
7/28/81
L 0.4
(n*l)
L 0.016
Phenanthrene
CM-254
30* Steel Storwdraln
E. End of Wheeler-Osgood
Waterway
0.29
(0.13-0.63)
(«•~)
3/29/82
15
0.036
Anthracene/
Phenanthrene
(combined)
L ¦ Less Than
NOTE: Low Molecular Might PAH have bean analyzed for, but not detected In, the following drains: CI-225(1), C1-234U), CI-243(1).
CI-245U), CI-24BU), and CI-703(1). The number In parentheses represents number of analyses. Detection limits In all cases ranged
frow 0.1 to 1 pg/1.
-------
Table 7.6.5
HIGH MOLECULAR WEIGHT PAH: SUMMARY OF LOADINGS
FROM DISCHARGES TO THE CITY WATERWAY
Drain #
Drain Nam
Flow (NGD)
(Avg and Range)
(f of Observations)
Period
of Observations
for Contaalnant
Concentrations
Concen-
tration (ug/1) Loading
(Avg and Range) (lbs/day)
(# of Observations) (Avg and Range)
Coapounds
Detected
CI-230
15th St. Storadraln,
48" Concrete Pipe
0.17
tO.14-0.22)
(n-3)
9/7/83
L 0.6
(n«l)
L 0.00085
Fluoranthene,
Pyrene, Benzo-
(g,h,1JPery1ene
CI-23*
24" Hood Box Outfall
at S. 21st Street
0.034
(0.03-0.037)
(n*2)
9/7/83
L 0.2
L 0.00057
Pyrene
CI-245
18" Concrete Pipe Stora-
draln froa Rlt Yard
0.070
(0.05-0.09)
-------
CITY WATERWAY
a flocculent was added to promote settling. Solids were retained for land
disposal (site not established) and the overflow was discharged to City
Waterway (NPDES Permit WA0001368).
Investigations of the D Street petroleum storage facilities have been
conducted by Johnson and Norton (1984b) and Hart-Crowser and Associates
(1982). The tank farms in this area of the waterway store leaded gasoline,
unleaded gasoline, and diesel fuel. Examination of groundwater has shown
contamination resembling these products and seepage of product from the
banks along the waterway. At high tide, this seepage is submerged and
the product bubbles to the surface creating a sheen. The contaminants
involved probably reach City Waterway sediments, but most undergo volatili-
zation and some dissolution because the product is dominated by one- and
two-ring compounds. The sediments off the D Street facilities were dominated
by four- and five-ring compounds, suggesting that the D Street facilities
was not a major source of LPAH or HPAH observed in the sediments.
In the upper waterway, the major storm drains are all confirmed PAH
sources, as demonstrated by the loading estimates. The presence of PAH
in these discharges is not surprising, given that the compounds are typical
constituents in urban runoff (Barrick 1982; Galvin and Moore 1982). The
sediment core data from Station CI-60 at the head of the waterway suggest
a historical source, possibly related to the coal gasification site at
23rd and A Streets (Tacoma Spur) that closed in 1926. According to Hart-
Crowser and Associates (1984), this site continues to contribute about
0.22 lb/day of total aromatic hydrocarbons to City Waterway via shallow
groundwater input. These investigators indicated that there were other
possible sources of groundwater contamination in this area, including an
abandoned gasoline station at Puyallup and A Streets, a coal- and wood-
fired power generating station, a machinery and equipment storage yard,
and source petroleun product storage tanks east of the waterway. PAH contamina-
tion has been found in soils beneath all but the power generating plant
site. This site was discovered while routine soil borings were being taken
for the SR-705 highway project.
The Tar Pits site is another potential source of PAH to Wheeler-0sgood
and City Waterways. The site consists of a group of scattered and undefined
ponds filled with liquid tar. The material 1s a waste product of a coal
gasification plant that operated on the site from 1924 to 1950. A sample
of the tar was analyzed and 1t was determined to contain four percent PAH.
Two additional sources of LPAH were discovered near the head of City Waterway.
One was in the vicinity of West Coast Grocery and the other was near 15th
Street. Petroleum product was collecting 1n storm drains near West Coast
Grocery and discharging to City Waterway via CI-248. The source of the
petroleun product (oils) 1s unknown but may be associated with the historical
operation of a railroad roundhouse 1n this area. Petroleum product (gasoline)
was discovered by the Washington State Department of Transportation (WDOT)
on the west side of City Waterway near 15th Street during field Investigations
for the proposed freeway right-of-way. The source of the gasoline 1s unknown
but WDOE Identified four gasoline stations 1n the vicinity that are over
20 yr old (Pierce, R,, 2 August 1985, personal communication). The Chevron
7.207
-------
CITY WATERWAY
facility may also be a potential source of LPAH to Wheeler-Osgood and City
Waterways.
Two sources of PAH to the waterway that could not be adequately assessed
with existing data are spills and atmospheric deposition. Spills and other
unauthorized discharges could represent a significant source of LPAH to
City Waterway, although most would be volatilized or degraded. A review
of recent WDOE spill records indicated that from 1979 to 1985, 3,500 -
4,000 gal of diesel, gasoline, or other petroleum products were released
into the water column of City Waterway. This does not include unreported
spills or discharge of PAH from activities such as bilge pumping, a practice
made illegal in the mid-1970s.
Atmospheric deposition is a potential route of PAH migration to the
waterway, particularly for HPAH. The importance of this route can only
be partially assessed because the Puget Sound Air Pollution Control Authority
(PSAPCA) does not collect data on PAH concentrations of airborne particulates.
The potential surface area available for direct deposition of particles
in the waterway is much less than that on land. Most of the PAH released
to the atmosphere would be expected to reach the waterways by surface runoff,
and therefore, should be accounted for in PAH loading estimates for the
drains. However, the largest concentration of PAH-contaminated material
can be expected to be discharged from the storm drains during the early
stages of a rainfall event, a period for which little contaminant monitoring
data exist. This may help explain why HPAH have been undetected in several
analyses of the storm drains.
Sources of dibenzofuran are unknown. Judging from the similarity
between dibenzofuran and PAH distributions in sediments, the same sources
are probably involved.
7.6.4.4 Summary and Recommendations--
The sources of LPAH and HPAH to the City Waterway are not well defined.
Several possible sources include:
t Storm drains - Based on the available loading data, the
storm drains are confirmed sources of LPAH and HPAH.
t D Street petroleum facilities - The petroleum storage facilities
on the east shore of City Waterway are known to be a source
of PAH to the waterway via groundwater as a result of past
spills and product leakage. However, the PAH contributed
by these facilities are dominated by one- and two-ring compounds
that do not persist in waterway sediments.
• Fick Foundry, Woodworth and Company, and marina fires -
These are suggested as potential past sources of HPAH to
City Waterway sediments.
7.208
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CITY WATERWAY
• Several facilities near the intersection of 23rd and A Streets
- Past facilities, including a coal gasification plant,
are potential historical sources of LPAH and/or HPAH and
ongoing sources of LPAH via groundwater, (i.e., the Tar
Pits site and the Tacoma Spur).
• Unknown sources of LPAH near the head of City Waterway -
Potential ongoing sources include Chevron, and unknown sources
near West Coast Grocery and 15th Street.
• General - Release of petroleum products from marinas, boats,
spills are potential sources.
LPAH and HPAH sources in Segment 3 near the mouth of City Waterway
need to be further explored. Properties along both sides of the waterway
should be inspected in order to identify potential sources. Additional
sediment sampling in the waterway may be valuable, particularly along the
western shore near the mouth, because all presently available data in this
area are limited to the central channel or eastern shore.
7.6.5 Dichlorobenzenes
7.6.5.1 Spatial Distribution--
Dichlorobenzenes were preliminary contaminants of concern in both
City and Wheeler-Osgood Waterways. In City Waterway, concentrations of
total dichlorobenzenes ranged from 47 to 400 ug/kg dry weight (600 to 3,300
ug/kg T0C), with an overall decrease in concentration from the head to
tne mouth of the waterway. The distribution of 1,4-dichlorobenzene is
shown in Figure 7.6.11. No historical data for 1,4-dichlorobenzene are
available.
The highest concentration of 1,4-dichl orobenzene normalized to both
dry weight and T0C was found at the head of City Waterway (Station CI-11).
A second maximum of l,4-d1chlorobenzene concentrations (dry weight) was
observed in the Wheeler-Osgood Waterway. Dry-weight concentrations decreased
in the main waterway in both directions from the juncture with Wheeler-
Osgood Waterway. A similar trend was observed when concentrations were
normalized to organic carbon content (Figure 7.6.11), except that there
was more scatter in the data and a relatively high concentration of 1,4-
dichlorobenzene near the mouth of City Waterway (Station CI-22). After
normalization to organic carbon, 1,4-d1chlorobenzene concentrations in
Wheel er-Osgood Waterway were lower than those 1n the main portion of City
Waterway. This relative difference suggests that a major source of 1,4-di-
chlorobenzene to City Waterway 1n this area was along the main waterway
rather than within Wheeler-Osgood Waterway.
1,2-Dichlorobenzene concentrations were elevated 1n Wheel er-Osgood
Waterway only when normalized to dry weight or organic carbon content (Figure
7.6.12). These data suggest a localized source of contamination that did
not affect the main channel of City Waterway. One possible explanation
7.209
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1.6
1.4
1.2
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0.8
0.6
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Benthlc effects
AET > 16000 ppb
(not established)
Toxicity
AET
(B)
(Thousands)
Ft. from mouth of watsrway
~ Tttr# 1«ch InvtitlgiUon • Qu»ntiuted v«luc
4 Tttr* T»ch Invcstlgifion - Und«tKt«d value
Figure 7.6.11
SURFICIAL SEDIMENT CONCENTRATIONS OF 1,4-DICHL0R0BENZENE
IN CITY WATERWAY, (A) DRY WEIGHT BASIS, (B) NORMALIZED
TO TOTAL ORGANIC CARBON
7.210
-------
Segment:
35C
300
250
200 -
150
100 -
50
~ o
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1 2
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2 4 6
(Thousands)
Ft. from mouth of waterway
(A)
Benthie effects
•nd toxicity
AET
Segment:
3.4
3.2 -
3 -
2.8 -
2.6 -
2.4 -
2.2 -
2 -
1.8
1.6 -
1.4 -
1.2 -
1 -
0.8 -
0.6 -
0.4
0.2 H
0
1 2
«
-1 1 I I r-
2 4 6
(Thousands)
Ft. from mouth of waterway
Benthic effects
•nd toxicity
AET
(B)
~ Tetri Itch Investigation - Quintltlted vilue
~ Tetrt Itch Investigation - Undetected vtlut
Figure 7.6.12
SURFI CIAL SEDIMENT CONCENTRATIONS OF 1,2-DICHLOROBENZENE
IN CITY WATERWAY, (A) DRY WEIGHT BASIS, (B) NORMALIZED
TO TOTAL ORGANIC CARBON
7.211
-------
CITY WATERWAY
for the substantially different distributions of these two dichlorobenzene
isomers is that 1,4-dichlorobenzene is transported from a source in City
Waterway to sediments in Wheeler-Osgood Waterway but that 1,2-dichloro-
benzene from a source in Wheeler-Osgood Waterway is not transported in
the opposite direction. A second, and perhaps more likely, explanation
is that there is little transport between the two waterways in either direction
because of a sill at the entrance of Wheeler-Osgood Waterway and that indepen-
dent sources of dichlorobenzenes (one enriched with 1,2-dichlorobenzene
in Wheeler-Osgood Waterway) contribute to the contamination observed in
each area.
In summary, there are distinctive differences in the composition of
chlorinated benzene contamination in City and Wheeler-Osgood Waterways.
In Wheeler-Osgood Waterway (City Waterway Segment 2), a major source of
1,2-dichlorobenzene is indicated, although 1,4-dichlorobenzene is also
present in smaller concentrations. In the main portion of City Waterway,
two sources of 1,4-dichlorobenzene are indicated when concentrations were
normalized both to dry weight and organic carbon content: (1) at the head
of the waterway, and (2) at about 4,700 ft from the mouth. A third source
near the waterway mouth is suggested on the basis of organic carbon-normalized
concentrations.
The vertical patterns of contamination in sediment core samples from
City Waterway are shown in Figure 7.6.13. For 1,4-dichlorobenzene, the
dissimilarity of the vertical contamination gradients among the cores indicates
that historically there was more than one source of the compound, and that
discharges have not been uniform throughout the waterway. At the head
of the waterway (Station CI-60), concentrations of 1,4-dichlorobenzene
increased over time, reached a maximum during the period represented by
deposition of the second horizon (0.3-0.6 m), and since that period have
decreased. This same vertical pattern of contamination was not apparent
in a core taken in the lower one-third of the waterway (Station CI-61).
In Wheeler-Osgood Waterway (0.5-m core, Station CI-62), concentrations
of 1,4- and 1,2-dichlorobenzene decreased only slightly with depth in samples
from a sediment core. However, similar to the pattern observed for PAH,
dichlorobenzene concentrations 1n both sediment core Intervals were 4-5
times greater than those observed in either of the surface (0-2 cm) sediment
samples from Wheeler-Osgood Waterway. This difference suggests that any
ongoing contaminant discharges are less than the historical discharges.
These data would be consistent with a slow sedimentation rate in Wheeler-
Osgood resulting in slow burial of contaminated sediments so that only
a thin layer at the surface reflects a reduced contaminant discharge.
7.6.5.2 Loading Estimates--
The following discharges have been sampled for chlorinated benzenes,
but the compounds have not been detected:
7.212
-------
on (ug/Kg-dry wight)
100
Concentrat
1000
10,000
0.4
0.6
E
1,4-01chlorobenzene AET
1,2-DIchlorobenzene AET
Concentration lug/Kg-dry weight)
0 10 100

t! 0.6
(B)
No AET exceeded 1n this core
•••• 1,2-dichlorobenzene
1,4-dichlorobenzene
Figure 7.6.13 (A and B)
CONCENTRATIONS OF 1,2-DICHLOROBENZENE AND 1,4-DICHL0R0BENZENE
WITH DEPTH IN THE SEDIMENT COLUMN, (A) STATION CI-60, 605;
(B) STATION CI-61, G01
7.213
-------
Concentr»tion (yg/Kg-dry weight)
100 1000 10,000
1
1
1

(C)
AET for both chemicals exceeded in this core.
Concentration (ug/Kg-dry weight)
10 100
0.1
J 0.2.
c
0.3
i
0.4 J
1,2-dichlorobenzene
- 1,4-dichlorobenzene
1000
' ¦ i ¦¦ 1 1 ».11 1—1—1 "l
: |
—i
• i
! 1
!
: 1
• u i
• 1
1 j
(D)
1,4-dichlorobenzene AET
1,2-dichlorobenzene AET
Figure 7.6.13 (C and D)
CONCENTRATIONS OF 1,2-DICHLOROBENZENE AND 1,4-DICHLOROBENZENE
WITH DEPTH IN THE SEDIMENT COLUMN, (C) STATION CI-62, B02:
(D) STATION CI-63, B01
7.214
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CITY WATERWAY

No. of
Detection

No. of
Detection
Drain
Sample
Limit
Drain
Sample
Limit
No.
Analyses
(ug/L)
No.
Analyses
(ug/L)
C1-225
2
1.0
CI-248
2
1.0
CI-230
3
1-10
CI-703
1
1.0
C1-234
1
1.0
CN-237
7
0.5-10
C1-243
2
1.0
CS-237
3
1-10
C1-245
2
1.0
CW-254
4
1-10
Refer to Figure 7.6.2 for drain numbers and locations along the waterway.
7.6.5.3 Source Identification--
Because there are no documented dischargers of chlorinated benzenes
to City Waterway, source identification efforts were based on probable
use of the compounds. The chlorinated benzenes are used as fumigants and
insecticides (Hawley 1981). 1,4-Dichlorobenzene is used as an air deodorant
and toilet bowl deodorant. 1,2-Dichlorobenzene is used as a solvent for
organic materials, a degreaser for hides and wool, and a solvent for oxides
of nonferrous metals (Hawley 1981). Potential sources of dichlorinated
benzenes in Wheeler-Osgood Waterway and City Waterway are discussed separately
below.
Wheeler-Osgood Waterway (City Waterway Segment 2)—The known use of
1,2-dlchlorobenzene as a degreaser for hides and the distinctive signature
of chlorinated benzenes in Wheeler-Osgood Waterway suggest Carsten's Packing
Company and Hygrade Foods as potential sources. Carsten's, a slaughtering
house and meat packing plant, probably started operating in the 1920s.
The company began leasing to Hygrade Foods around 1955. Hygrade eventually
bought the company around 1960 (Brandt, C., personal communication). The
meat packing plant had been a major discharger of untreated process wastes
to the Wheeler-Osgood Waterway. The discharge of process wastes from Hygrade
dropped significantly about 1970 after connection with the city of Tacoma's
sanitary sewage system. However, as a result of unidentified cross-connections
between the process effluent and the cooling water/storm runoff system,
some discharge of process wastes to Wheeler-Osgood continued until at least
the mid-1970s. Hygrade Foods is currently permitted to discharge only
runoff noncontact cooling water to Wheeler-Osgood (Hygrade NPDES Permit).
The actual use and discharge of chlorinated benzenes by Carsten's
Packing Company/Hygrade Foods has not been documented. A retired Hygrade
employee (Brandt, C., personal communication) does not recall the use of
chlorinated benzenes at Hygrade Food. In view of the known use of l,2-d1chloro-
benzene as a degreaser for hides, this compound could be associated with
this industry. According to D. Nelson (personal communication) of Frontier
Leather Company, the tanning industry commonly used chlorinated benzenes
as fuglcldes on hides prior to 1961. Since that time, salt has been more
commonly used. No other known or potential sources of chlorinated benzenes
to Wheeler-Osgood Waterway have been Identified.
7.215
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CITY WATERWAY
City Waterway (Segments 1 and 3)--The proportion of 1,4-dichlorobenzene
relative to 1,2-dichlorobenzene was greater in sediments from City Waterway
than in those from Wheeler-Osgood Waterway. This difference suggests a
separate source in chlorinated benzenes in City Waterway.
Use of chlorinated benzenes by industries along the waterway could
not be confirmed. Inquiries were made of plywood manufacturers (Puget
Sound Plywood) and shipbuilders (Todd Shipyards) to determine whether this
compound class is commonly used as a solvent in an industrial process,
but they were unsuccessful.
Potential use of chlorinated benzenes by the Burlington Northern Railroad
car washing yard on East 21st Street was investigated. According to Dames
and Moore (1982), waste materials from this operation including solvents,
chemicals, and oil, were disposed of on the ground at this site. However,
a review of WDOE files indicated that the car washing yard is probably
not a source of chlorinated benzene contamination to the City Waterway.
According to the Burlington Northern's 1972 NPDES application, box cars
containing only grain, lumber, canned goods, fertilizer, and a variety
of food products are washed. The cars are cleaned with city water, and
the effluent is discharged to the Puyallup River. Only the engine house
area discharges to City Waterway. While it cannot be established with
certainty that toxic chemicals were never handled at the car washing yard,
it is assumed that the discharge always went to the Puyallup River and
would not be associated with contamination in City Waterway. Discharge
from the Burlington Northern engine house has historically been routed
through an outfall at the head of City Waterway. If dichlorlnated benzenes
were used as solvents at this facility, they would have probably been released
to City Waterway via this outfall. (It was not established during these
investigations whether the engine house still exists; Burlington Northern's
1972 NPDES application indicated that it was scheduled for removal.)
The areas of elevated 1,4-dichlorobenzene concentrations (the head
of City Waterway and 4,700 ft from the mouth) suggest possible input via
the Nalley Valley, south Tacoma, and 15th Street drains. Alhough effluent
sampling has failed to detect any dichlorlnated benzenes from these discharges,
these outfalls may be historical or intermittent sources of the compounds.
7.6.5.4 Summary and Recommendations-
Chlorinated benzenes are preliminary contaminants of concern 1n Segments
1, 2, and 3. The relative proportion of 1,2- and 1,4-dichlorobenzene in
Segment 2 was different from that 1n Segment 1 and 5. This signature existed
in both surfldal sediments and deep cores, indicating separate sources
of chlorinated benzenes in Wheeler-Osgood Waterway and the main portion
of City Waterway.
The origin of chlorinated benzenes 1n Wheeler-Osgood Waterway is unknown.
There is no evidence that 1,2-d1ch1orobenzene was used 1n the curing or
tanning of hides at Carsten's Packing Company or Hygrade Foods. The presence
of chlorinated benzenes in surficlal sediments of Wheeler-Osgood Waterway
7.216
-------
CITY WATERWAY
suggests that contamination may be ongoing, but concentrations in 0-2 cm
surface sediments were several times less than those observed in the two
composited intervals (0-14 and 14-43 cm) of a core from the same area.
A similar difference was noted for the main channel of City Waterway.
The maximum 0-2 cm sediment concentration of 1,4-dichlorobenzene (290 ug/kg
dry weight; Station CI-11) was less than 15 percent of the corresponding
value for the 0-30 cm interval of the core collected in the same area.
These data suggest that the dichlorobenzene load may have recently decreased
in both City and Wheeler-Osgood Waterways.
Possible sources of chlorinated benzenes to the main portion of City
Waterway include the Burlington Northern engine house and the drains of
Nalley Valley, south Tacoma, and 15th Street. None of the sources can
be confirmed.
The following recommendations may help focus further description of
chlorinated benzene sources:
• Investigate Hygrade Foods and other properties with discharge
via the Wheeler-Osgood drain to determine if there is an
ongoing source of dichlorinated benzenes
• Investigate potential uses and sources of dichlorinated
benzenes in the areas drained by the Nalley Valley, south
Tacoma, and 15th Street drains.
7.6.6 4-Methylphenol
7.6.6.1 Spatial Distributlon--
Surficial sediment concentrations of 4-methylphenol (Figure 7.6.14)
ranged from 140 to 940 ug/kg dry weight (4,200 to 16,000 ug/kg T0C) in
Segments 1 and 3 of City Waterway, and were 1,200 ug/kg dry weight (11,000
ug/kg T0C) in Segment 2 (Wheeler-Osgood Waterway). On a dry-weight basis,
the area of greatest 4-methylphenol contamination was located between 3,700
and 4,700 ft from the mouth of the waterway (Stations CI-15, CI-17, CI-18).
When normalized to T0C, 4-methylphenol concentrations in sediments from
Stations CI-15, CI-17, and CI-18 remained high and those in sediments from
the mouth of the waterway were also elevated. This pattern of contamination
suggests a source between 3,700 and 4,700 ft from the waterway mouth and
a second source at the mouth of City Waterway. The extent of contamination
in Wheel er-Osgood Waterway 1s unclear given the variability of 4-methyl-
phenol concentrations in the two samples taken [i.e., 270 ug/kg in January,
1984 (Station CI-01) and 1,200 ug/kg 1n March, 1984 (Station CI-16)].
The variability may have arisen from differences 1n analytical protocols,
or from natural variability 1n the environment.
Throughout the waterway, concentrations of 4-methylphenol in sediment
cores were essentially uniform within each core (Figure 7.6.15). No other
compounds of concern in the waterway showed such homogeneity, presumably
because 4-methylphenol is among the most soluble of the compounds examined
7.217
-------
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0.3 -
0.2 -
0.1 -
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(Thousonds)
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Benthlc effects
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~ Tctrt Tech Jnv*st1(«t1ori • Qu«nt1t*ted v«lu»
~ Tftr* T«ch lnvtitlgttlon - undetected v«1ur
Figure 7.6.14
SURFICIAL SEDIMENT CONCENTRATIONS OF 4-METHYLPHENOL
IN CITY WATERWAY, (A) DRY WEIGHT BASIS, (B) NORMALIZED
TO TOTAL ORGANIC CARBON
7.218
-------
Concentration (yg/Kg-dry weight)
10
i i
100
¦ • ¦ ¦ 1
i i i ¦ >
1000
III. I
10,000
I % I I I
Benthlc effects—*!
and toxicity
AET
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|ci-63
B01
X •
CI -62
BO 2
CI-61
G01
CI-60
G05
Figure
CONCENTRATION OF
WITH DEPTH IN THE
AT STATIONS IN
4-METHYLPHENOL
SEDIMENT COLUMN
CITY WATERWAY
7.219
-------
CITY WATERWAY
and would therefore tend to migrate in the interstitial water. At every
site in the nearshore/tideflats area where 4-methylphenol was detected,
concentrations were nearly constant throughout the depth of all sediment
cores. Therefore, its vertical distribution in the sediment cores provides
little or no indication of the historical rate of contaminant input.
7.6.6.2 Loading Estimates—
The Nalley Valley drain (CN-237) is the only drain for which effluent
has been analyzed for 4-methylphenol. In two analyses in 1984, 4-methylphenol
was undetected at 1 ug/L (WDOE unpublished). There are no known permitted
discharges of phenol to City Waterway.
7.6.6.3 Source Identification--
4-Methylphenol (p-cresol) is a coal tar derivative used in the production
of phenolic resins, in ore flotation, and as a synthetic food flavoring.
Although not a priority pollutant, it is on U.S. EPA's list of hazardous
substances (U.S. EPA 1983c). Potential sources can be explored based on
industrial types and known uses of this compound class by industries along
the waterway.
Considerable wood debris was noted in sediments from Wheeler-Osgood
Waterway. It was concluded in Section 7.4.4.2 that the anoxic degradation
of wood chip debris in sediments is a possible source of alkylated phenols,
including 4-methylphenol. The actual contribution (if any) to the total
concentration of 4-methylphenol observed in Wheeler-Osgood Waterway sediments
may only be speculated.
4-Methylphenol may enter City Waterway via discharge of wastewater
containing phenolic resins used in plywood manufacturing. North Pacific
Plywood, located at 1549 Dock Street (5,900 ft from waterway mouth), has
manufactured plywood at this location since 1960 (Ruckelshaus 1985). The
facility was originally built by the North Pacific Railroad to manufacture
boilers for steam locomotives (Cook and Anderson 1983). According to Dames
and Moore (1982), this facility deposited glue wastes on land in an unknown
location, possibly on the property. The firm has a long history of spills
of phenolic resins at the site, the most recent in December, 1977. when
a hose from a tank truck ruptured and phenolic glue waste reached the waterway
(Monahan 1978). Due to numerous spills in the vicinity, the ground beneath
the glue tank had become saturated with phenolic resins, and the WDOE ordered
removal of contaminated soil (Docket No. DE 78-162). WDOE was notified
that contaminated soils had been removed on March 7, 1978. A storm drain
in the immediate vicinity of the glue tank may have provided a route for
spilled phenolic glues to reach the waterway since this drain was not sealed
during resin handling operations until 1977 (Hall 1977).
While spills of phenolic resins to the ground and subsequent direct
leaching to the waterway could be a source of 4-methylphenol to City Waterway,
this route 1s not reflected 1n the spatial gradient of contamination of
waterway sediments. Sediments at Station CI-14, located 1n the middle
7.220
-------
CITY WATERWAY
of the waterway off North Pacific Plywood, were less contaminated with
4-methylphenol than were many other City Waterway sediments.
The firm may have contributed to contamination of the waterway via
the storm sewer system. Station CI-15, with the greatest 4-methylphenol
contamination in City Waterway, is located near the outfall of the 15th
Street drain (CI-230). This storm drain serves 1 mi2 0f Tacoma (21st Street
to 8th Street, West to Grant Avenue, based on a map provided by the city
of Tacoma Department of Public Works). The storm drain in the immediate
vicinity of North Pacific Plywood's glue tank discharges through the 15th
Street drain. It appears likely that North Pacific Plywood contributed
phenols to City Waterway through this route.
Northern Pacific Plywood plant along City Waterway is being dismantled.
Manufacturing operations have been moved to Graham.
Other potential sources of phenols from the wood products industry
were investigated. Puget Sound Plywood is located at 230 East F Street,
on the tip of the point of land separating City and Middle Waterways (see
Figure 7.6.1). Phenolic glues have been spilled on the property (Dames
and Moore 1982) and phenol-contaminated glue wastes have been disposed
of on-site. Although contaminants originating from the site would probably
reach Commencement Bay rather than City Waterway, this facility may have
contributed to the 4-methylphenol contamination in sediments near the mouth
of the waterway.
Harmon Cabinets, presently located at 1933 Dock Street (see Figure
7.6.1), has been in business since the late 1800s. Records do not indicate
whether they have always been in business at this location on the waterway.
The firm is served by the same storm drainage network noted above for North
Pacific Plywood. It is unknown if phenolic resins are used in their furniture
manufacturing operations or 1f these materials have been released to the
environment. There 1s no evidence that Harmon Cabinets disposed of wastes
on-site to the ground, directly to the waterway, or through spills (Dames
and Moore 1982).
St. Regis Door Mill was a possible source of phenols to Wheeler-Osgood
Waterway. St. Regis Door Mill had an NPDES permit (WA0003221, expired 1/31/78)
to discharge to Wheeler-Osgood Waterway with limitations for oil and grease.
According to the U.S. EPA staff evaluation report on the application (10/19/73),
the oil and grease resulted from air compressor cooling water discharge.
If the facility used glues and resins 1n door manufacturing, improper waste
disposal may have contaminated the waterway. This facility 1s no longer
operating. Its closing date is not known.
As a coal tar derivative, 4-methylphenol may be expected in wastes
at the Tar Pits and Tacoma Spur (23rd and A Streets) coal gasification
sites. A tar sample from the Tar Pits site (2202 East River Street) showed
80 mg/kg 4-methylphenol and 30 mg/kg 2-methylphenol (Kennedy-Jenks Engineers
1983). These substances were not included 1n groundwater analyses conducted
at the Tar Pits site or at the Tacoma spur site (Hart-Crowser and Associates
7.221
-------
CITY WATERWAY
1984). Given the concentration of 4-methylphenol in the tar at Tar Pits,
the solubility of the compound, and the similarity of the materials buried
at the Tar Pits and the Tacoma Spur site, it is reasonable to expect the
compound to be found in the tar and groundwater at both sites.
Groundwater at the Tar Pits site appears to flow to the Puyallup River
rather than to City Waterway (Kennedy-Jenks Engineers 1983). Groundwater
from the Tacoma Spur site is expected to discharge to City Waterway south
of 21st Street, within 700 ft of the head of the waterway (Hart-Crowser
and Associates 1984). 4-Methylphenol concentrations in surficial sediments
within this area showed some elevation when normalized to dry weight, but
not when normalized to organic carbon. The Tacoma Spur site could be a
significant source of 4-methylphenol to City Waterway. However, the sediment
chemistry data available are inconclusive.
7.5.6.4 Summary and Recommendations-
Spatial distribution of 4-methylphenol in City Waterway indicates
a source in Segment 1 between 3,700 and 4,700 ft from the mouth of the
waterway and a possible second source near the mouth in Segment 3. Vertical
4-methylphenol concentrations were uniform in the sediment column.
The 15th Street drain (CI-230) is a possible source of 4-methylphenol
in Segnent 1. The highest levels of 4-methylphenol observed in City Waterway
sediments were observed in samples taken in the middle of the waterway
near this outfall. North Pacific Plywood, a plywood manufacturer and heavy
user of phenolic resins, was located (until 1983) within the drainage area
served by this storm drain. The firm had a history of spills at the site.
Spilled materials could have been transported to the waterway via the storm
drain located 1n the vicinity of the glue tanks. The plant has recently
closed and contamination from this source 1s presumed to be historical.
It 1s unknown whether there are other historical or ongoing sources of
4-methylphenol within the drainage area by the 15th Street drain. Discharges
and spills from Puget Sound Plywood at the mouth of the waterway may be
contributing to contamination of sediments at the mouth of the waterway.
The Tacoma Spur coal gasification site is probably a historical and
ongoing source of 4-methylphenol to City Waterway. At the present time,
groundwater from the site may contribute 4-methylphenol to City Waterway,
although the sediment quality data available provide only limited evidence
of its Impact. The Tar Pits site is a potential source of 4-methylphenol
to the Wheeler-Osgood and City Waterways via groundwater. Degradation
of buried wood chip debris may also contribute to the 4-methylphenol concen-
trations observed.
The following recommendations may help focus further description of
4-methylphenol sources:
• Investigate potential sources of 4-methylphenol within the
drainage area served by the 15th Street drain
7.222
-------
CITY WATERWAY
• Investigate the Tacoma Spur coal gasification site as a
source of 4-methylphenol to City Waterway via groundwater,
since there are no data available to indicate the extent
or magnitude of 4-methylphenol contamination on the property
• Investigate the Tar Pits site a source of 4-methylphenol
to Wheeler-Osgood and City Waterways via groundwater.
• Investigate the production of 4-methylphenol in decaying
wood debris as a potential source to Wheeler-Osgood Waterway
4-Methylphenol has a lower affinity for sediments and associated organic
material than do many of the other contaminants of concern in the nearshore/
tideflats area. Source control efforts should be particularly effective
because the compound would not be expected to persist in the sediments
if sources could be eliminated. This factor also suggests that removal
of contaminated sediments would not be an appropriate remedial action,
unless possible in situ degradation of wastes in the sediments produced
sufficient 4-methylphenol to be a problem over time.
7.6.7 Polychlorinated Biphenyls
7.6.7.1 Spatial Distribution--
The distribution of polychlorinated biphenyls (PCBs) in the surficial
sediments of City Waterway, based on the Tetra Tech surveys and all historical
data, is illustrated in Figure 7.6.16. PCB concentrations in surficial
sediments in City Waterway typically were below 200 ug/kg dry weight, with
the exception of data from historical surveys near the mouth of the waterway.
The two data points with elevated PCB concentration at about 2,300 ft from
the waterway mouth were those of Mai ins et al. (1980). In general, the
PCB distribution throughout the waterway was patchy, with no distinct pattern.
Two sediment core samples were available 1n Segment 1. In sample
CI-63, approximately 4,700 ft from the waterway mouth, PCBs were undetected
at 100-110 ug/kg throughout the core. In core C1-60 at the head of the
waterway. PCB concentrations Increased with depth in the sediment and then
decreased in the lowest horizon (Figure 7.6.17). The elevation in concentration
at depth in sediment from Segment 1 indicates that historical input is
greater than present input. In the deep core 1n the lower waterway (CI-61),
PCBs were undetected at 70-90 ug/kg throughout the core.
7.6.7.2 Loading Estlmates--
PCBs have never been detected in storm drain discharges to City Waterway.
The following outfall discharges have been analyzed for PCBs:
7.223
-------
Segment:
700
c.
g>
*
TJ
X.1
a
a.
n
v
3
O
>
¦o
•>
v
c
o
o
600 -
500 -
400 -
300 -
200
100 -
~ ~
93
lo.

e
T"
2
"T
Ft.
1 1 -r-
4 6
(Thousands)
from mouth of waterway
(Benthlc effects
AET
not exceeded)
Toxicity
AET
(A)
o
o
.o
a
a
§> n
si
0 O
>5
1 ?
V
(I
o
c
o
u
Segment:
21
20
19 -
18 -
17 -
16 -
15
14 H
13
12
11 -
10 -
9 -
8 -
7
6
5
4
3
2
1
0
1 2
a
a o
-i 1 1— 1 r-
2 4 6
(Thousands)
Ft. from mouth of waterway
(no AET exceeded)
(B)
~ Tetri Tech Investigation - Quint 1tlted Value
0 Other ]nveit1get1oni - Quant Hit td Value
A Tetre Tech Investigation - Less Than Value
V Other Investigations - Lett Thin Vilu*
~ Tetra Tech Investigation - Undetected Value
X Other Investigation - Undetected Value
Figure 7.6.16
SURFICIAL SEDIMENT CONCENTRATIONS OF PCBs
IN CITY WATERWAY, (A) DRY WEIGHT BASIS, (B) NORMALIZED
TO TOTAL ORGANIC CARBON
7.224
-------
Concentration (yg/Kg-dry weight)
10
100
i i i 11111
i i
1000
11 III
L- oxlclty
AET
i
I
data not reported
• BentMc effects AET of 1100
I ug/kg DW not exceeded
Figure 7.6.17
CONCENTRATION OF PCBs WITH DEPTH IN THE
SEDIMENT AT STATION CI-60, 605 NEAR
THE HEAD OF CITY WATERWAY
u = undetected at concentration shown
7.225
-------
CITY WATERWAY

Detection

Detection
Drain
Sample
Limit
Drain
Sample
Limit
No.
Analyses
fuq/L)
No.
Analyses
(uq/L)
C1-225
1
0.5-2.0
CI-248
1
0.5-2.0
C1-230
2
0.1-2.0
CI-703
1
0.5-2.0
C1-234
1
0.5-2.0
CN-237
7
0.05-2.0
C1-243
1
0.5-2.0
CS-237
2
0.5-2.0
C1-245
1
0.5-2.0
CW-254
3
0.5-2.0
Although these measurements cannot be considered complete, they indicate
that PCBs are not presently discharged via storm drains 1n measurable quanti-
ties .
7.6.7.3 Source Identification--
The absence of clear spatial gradients in the surficial sediment data
and the lack of discharge data related to PCBs complicates source identifi-
cation. PCBs are used in heat-exchange and insulating fluids in transformers,
paints, and hydraulic oils (Young et al. 1979). Their manufacture was
banned in 1976. Based on their use in transformers, PCBs may be present
on properties occupied by industries with a high electrical demand. The
industries surrounding City Waterway in the area of greatest PCB contamination
include a furniture manufacturer, a plywood manufacturer (now closed),
a roofing contractor, a shipbuilder, a plywood distributor, a grocery warehouse,
and a railroad yard. None of these facilities is known to handle large
amounts of PCB-contaminated material, nor has there been any known release
of PCBs from these firms.
There is no known release of PCBs through drains entering the waterway,
and there is no gradient of sediment contamination to implicate any of
these drains as a source.
Spills of PCBs to City Waterway have not been reported in the last
7 yr (WDOE Environmental Complaint files 1979-1985).
7.6.7.4 Summary and Recommendations—
PCB levels 1n surficial sediments of City Waterway were variable with
no apparent gradients. Historical measurements at about 2,500 ft from
the Waterway mouth indicated concentrations ranging from 200 to 700 ug/kg
dry weight. No defined hot spots were identified in the recent data.
Available data Indicate that PCBs occur throughout the waterway at variable
levels. It was not possible to Identify the source of this contamination.
A reconnaissance survey may be helpful in Identifying potential PCB sources.
7.226
-------
CITY WATERWAY
7.6.8 Copper and Zinc
7.6.8.1 Spatial Distrlbution--
Surficial sediment concentrations (dry weight) of copper and zinc
in City Waterway showed similar spatial trends. The spatial gradients
of contamination along the length of the waterway are shown in Figure 7.6.18,
using data from the Tetra Tech 1984 survey and all available historical
sediment data. Concentrations generally decreased from the head of the
waterway to the mouth for both copper and zinc. Concentrations in sediments
from several stations at 4,500-5,000 ft from the waterway mouth were elevated
relative to those elsewhere in the waterway, up to a maximum of 2,100 mg/kg
dry weight for each metal. These stations were located along the eastern
shore of the waterway in the vicinity of Martinac Shipbuilding and were
sampled by Norton and Johnson (1984). Concentrations of copper and zinc
were also elevated in Wheeler-Osgood Waterway, but to a lesser extent than
along Martinac Shipbuilding. Normalization of these data to percent fine-
grained material did not indicate other trends.
Sediment core data from a station at the head of the waterway (CI-60)
are illustrated in Figure 7.6.19. Copper concentrations showed a slight
increase (i.e., factor of 1.5) with depth in the sediment down to 1.3 m.
The copper concentrations in surface sediments (0-2 cm) from this area
were similar to that in the top 30 cm interval of the core. Zinc concentrations
were also similar between the 0-2 cm surface sediment sample and the 0-30 cm
sediment core interval, but increased fivefold with depth down to 1.3 m.
Below 1.3 m, the concentrations of both copper and zinc decreased abruptly.
From these data it appears that after an initial buildup, the input of
copper has decreased only slightly over time while that of zinc has decreased
significantly.
The spatial pattern of metals contamination suggests that a major
source of metals is located at the head of City Waterway. The data of
Norton and Johnson (1984) also indicate a source along the eastern shore
of the waterway, approximately 4,500-5,000 ft from the mouth. A source
is also possible 1n Wheeler-Osgood Waterway, although data are not conclusive.
7.6.8.2 Loading Estimates-
There are currently no NPDES-permitted discharges of copper or zinc
to City Waterway. Prior to 1978, American Plating (at one time known as
Puget Sound Plating) had an NPDES permit to discharge process effluent
directly to the waterway, although the firm currently discharges process
wastewaters to the city sanitary sewer system.
Storm drain discharges have been sampled on a number of occasions
over the last 4 yr to determine metal loadings. Results are summarized
1n Tables 7.6.6 and 7.6.7. Copper was found in five drains. The largest
input (2.0 lb/day) was found in the south Tacoma drain (CS-237). The Nalley
Valley drain (CN-237, 0.84 lb/day) and the 15th Street drain (CI-230, 0.3
lb/day) were also major contributors of copper. Zinc was found in 10 drains.
7.227
-------
Segment:
700
£
o»
X
*
•D
E
Q.
a
m
4>
3
I
"O
w
M
O
c
o
o
600
500 -
400
300 -
200 -
100 -

«
1
•
1
•
1
1
•
•
1
t
1
1
1
1
1
•
1
1
1
1
1
1
1
1
1
1
1
1
1
•
:
»
~
~
•
a o
o* o
~ i
a 1
1
tP-$- tj
2,160 ppoi
6
-------
0
Concentration (mg/Kg-dry weight)
100 1000 10,000
¦ ¦ ¦ ¦' I I I I I ¦ 11 i I '
(A)
-Benthlc effects
and toxicity
AET
100
-lJ
1000
i-kJ
10,000
I_LJJ
¦t-4
i i
Toxicity
AET
Benthlc•
Effects
AET
(B)
Figure 7.6.19
CONCENTRATION OF (A) COPPER, AND (B) ZINC WITH
DEPTH OF SEDIMENT AT STATION CI-60, G05 NEAR
THE HEAD OF CITY WATERWAY
7.229
-------
Table 7.6.6
COPPER: SUMMARY OF LOADINGS FROM DISCHARGES TO THE CITY WATERWAY

Drain #
Drain Name
Flow (MGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)

CI-230
15th Street storm drain,
48" concrete pipe
0.17
(0.14-0.22)
("•3)
4/28/82-11/21/83
210
(7-420)
(n-2)
0.30
(0.0099-0.60)
C1-234
24" mod box outfall
at South 21st Street
0.034
(0.03-0.037)
(n-2)
11/21/83
34
(n-i)
0.0096
CI-248
18" concrete pipe,
850 ft south of
15th Street
0.020
(0.01-0.03)
(n-2)
11/21/83
10
(n«l)
0.0017
CN-237
Nalley Valley Drain
3.6
(1.2-10.66)
(n-8)
7/28/81 - 10/26/83
28
(6-60)
(n-5)
0.84
(0.18-1.8)
CS-237
South Tacoma Drain
4.8
(2.58-10.98)
(n"4)
2/16/82
50
(n-1)
2.0
CW-254
30" steel storm drain
east end of Wheeler-
Osgood Waterway
0.29
(0.13-0.63)
(n-4)
7/28/81-11/7/83
24
(10-40)
(n-3)
0.058
(0.024-0.097)
MOTE: Copper has been analyzed for but not detected 1n the following drains CI-225(1), CI-243(1), CI-245(1), CI-703(1),
CS-237(2) (the number 1n parentheses represents number of analyses). Detection limit for all samples Mas 1 ug/1.
r.230
-------
Table 7.6.7
ZINC: SUMMARY OF LOADINGS FROM DISCHARGES TO THE CITY WATERWAY
Drain 1
Drain Kame
Flow (MGD)
(Avg and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (vg/l)
(Avg and Range)
(# of Observations)
Loading
(lbs/day)
(Avg and Range)
CI-255
36" Concrete Stormdraln
under 11th St. Bridge
0.051
(0.032-0.07)
(n-2)
9/7/83-11/21/83
11
(9-12)
(n-2)
0.0046
(0.0038-0.0051)
CI-230
15th St. Stormdraln,
48" Concrete Pipe
0.17
(0.14-0.22)
(n-3)
4/28/82-11/21/83
170
(38-365)
(n«3)
0.24
(0.54-0.52)
CI-234
24" Wood Box Outfall
at S. 21st Street
0.034
(0.03-0.037)
(n-2)
9/7/83-11/21/83
20
(15-25)
(n-2)
0.0057
(0.0043-0.0071)
CI-243
21" Steel Pipe Stormdraln
from RR Yard
0.37
(0.21-0.52)
(n«2)
9/7/83-11/21/83
35
(16-54)
(n-2)
0.11
(0.049-0.17)
CI-245
IB" Concrete Pipe Storm-
draln from RR Yard
0.070
(0.05-0.09)
(n-2)
9/7/83-11/21/83
30
(10-50)
(n-2)
0.018
(0.0058-0.029)
CI-248
18" Concrete Pipe, 850 ft
S of 15th Street
0.020
(0.01-0.03)
(n-2)
9/7/83-11/21/83
33
(30-35)
(n-2)
0.0055
(0.0050-0.0058)
CI-703
Concrete Pipe Drain at
Harmon's Furniture
0.075
(0.06-0.09)
(n-2)
9/7/83-11/21/83
9.0
(n-2)
0.0056
CN-237
Nalley Valley Drain
3.6
(1.2-10.66)
(n«8)
7/28/81-4/17/84
47
(2-180)
(n«8)
1.4
(0.15-5.4)
CS-237
South Tacoma Drain
4.8
(2.58-10.98)
(n-4)
9/7/83-11/21/83
29
(2-80)
(n«3)
1.2
(0.080-3.2)
CH-254
30" Steel Stormdraln
E End of Wheeler-Osgood
Waterway
0.29
(0.13-0.63)
(n-4)
7/28/81-11/7/83
79
(42-140)
(n-4)
0.19
(0.10-0.34)
7.231
-------
CITY WATERWAY
The largest loading (1.4 lb/day) was calculated for the Nalley Valley drain
(CN-237). The south Tacoma and the 15th Street drains contributed 1.2
and 0.24 lb/day of zinc, respectively. There was also a substantial discharge
of zinc (0.19 lb/day) from the storm drain at the head ofthe Wheeler-Osgood
Waterway (CW-254). Care should be taken in interpreting the loading data
in Tables 7.6.6 and 7.6.7 due to the small sample sizes and the poor character-
ization of contaminant discharges during storm events. Data from the Nalley
Valley drain (CN-237) were better than other data, but those for a complete
storm event were not available.
Most of the information pertaining to the concentration of metals
in discharges to City Waterway has been collected since 1981. However,
until 1979, untreated combined storm and sanitary sewers discharged directly
to City Waterway, carrying domestic and industrial wastes (see Section
7.6.3). Therefore, it seems likely that historical metals loading from
discharges to City Waterway may have been greater than indicated by the
recent data available.
7.6.8.3 Source Identification--
Storm drains, particularly the Nalley Valley/south Tacoma drains,
appear to be the major sources of metals to City Waterway based on the
sediment chemistry and loading data. Martinac Shipbuilding and American
Plating are also potential sources. These three sources are addressed
Individually below.
Storm Drains—Storm drains accounted for a metals loading of 3.2 lb/day
copper and 3.2 lb/day zinc to.City Waterway. Most of the loading (88 and
81 percent copper and zinc, respectively) was attributed to the south Tacoma
and Nalley Valley drains at the head of the waterway. These two drains
serve portions of the 1-5 corridor, the Nalley Valley, and south Tacoma
to South 80th Street along Pacific Avenue (Figure 7.6.20). Although effluent
from these drains 1s principally runoff, there may still be some unidentified
industrial discharges to these sewer systems. The magnitude of potential
unpermitted Industrial input cannot be established.
Urban runoff probably accounts for much of the discharge of copper
and zinc to the head of City Waterway. Wiglngton et al. (1983) indicate
that zinc particulates result from tire wear (zinc 1s used as a binding
agent 1n automobile tires). The metal 1s also found 1n motor oil. Copper
is found 1n brake linings (Wiglngton et al. 1983) and antifreeze (up to
76 mg/L). Antifreeze 1s comnonly dumped down storm drains when local residents
change antifreeze 1n their radiators or perform other auto maintenance
tasks. Particulate copper from brake lining wear would be washed into
the storm sewer during storms and street sweeping operations. Corrosion
of copper- and z1nc-galvan1zed plumbing probably also adds metals to urban
runoff (Cle et al. 1984). The primary source of zinc to the environment
1s the weathering and abrasion of galvanized Iron and steel (Galvln and
Moore 1982). In western Washington, where the water 1s naturally soft,
this corrosion could represent a substantial source. With the separation
of storm and sanitary sewers, discharges from this source should be reduced,
7.232
-------
r
s
HH
iBl-VBil I'm
!a«cT~»rn
mmrrmm
iKMitniBmi
[¦¦ra»rai
FET!BifTS
I t
s
jnrawrra
nan
nrrrTT*
nm*Ti
cszilmses^
E 11 Hlft
44TJ IT.
STPH)
cni
GUM
! *T®\
on a
¦I flit! H
APPROXIMATE DRAINAGE AREA
SERVED BY THE NALLEY VALLEY AND
SOUTH TACOMA DRAINS

I win
7.233
-------
CITY WATERWAY
although there may still be some contribution from unidentified process
discharge connections or from noncontact cooling water discharges to the
storm sewer system.
The range of values obtained during sampling of the City Waterway
drains indicate that time of sampling and type of sample are important
in obtaining representative contaminant loading data. Only 1-6 percent
of copper and 0.8-8.0 percent of zinc are soluble (Wigington et al. 1983);
both contaminants will be transported primarily in the particulate phase.
It is possible to measure high concentrations during the first flushing
of the sewer during a storm, but, as flows increase, loading of contaminants
may increase even as concentrations begin to decrease (Helsel et al. 1979).
For this reason, the February 16, 1982 storm sampling of the Nalley Valley
and south Tacoma drains showed 74 and 320 mg/L TSS with correspondingly
high flows and metals concentrations, and therefore high loadings of copper
and zinc (Norton and Johnson 1984). In contrast, samples of effluent from
these same drains collected November 21-22, 1984 following 6 days of rain
had <1 mg/L TSS in both drains, concentrations of zinc were low, and copper
was undetected. Despite the uncertainties 1n the loading data, the Nalley
Valley and south Tacoma drains are the major sources of copper and zinc
to City Waterway.
Martinac Shipbuilding—The highest concentrations of metals reported
in City Waterway sediments were found along the waterfront adjacent to
Martinac Shipbuilding (Norton and Johnson 1984). Located just north of
15th Street, Martinac Shipbuilding has been building and repairing ships
at this site since 1924. Both sandblasting grit and antifouling paints
may be sources of zinc- and copper-contaminated materials to the waterway.
A coarse-grained black sand with high metal concentration levels was found
just offshore of the Martinac property (Norton and Johnson 1984). Subsequent
investigation revealed that a sandblasting material known as "Tuf-Kut"
is used at this facility. Information supplied by the manufacturer Indicates
that this blasting sand contains 1,300-5,000 mg/kg copper and 75 mg/kg
zinc. Concentrations of these contaminants 1n nearby waterway sediments
were 2,160 mg/kg copper and 2,100 mg/kg zinc (Norton and Johnson 1984).
It is also possible, although not confirmed, that Martinac Shipbuilding
used granulated ASARC0 slag as sandblasting material, as had been common
in the Tacoma area (Norton and Johnson 1984). ASARC0 slag "typically"
has 5,000 ppm copper and 18,000 ppm zinc (ASARC0 1971).
Antifouling paints use any of several trace metals as toxic agents.
Copper is a coirmon constituent 1n these paints. At a ship building/repairing
facility such as Martinac, antifouling paints would be removed from boat
hulls during sandblasting operations. These paints could represent a signifi-
cant source of copper and other metals (e.g., cadmium and tin) if permitted
to enter the waterway.
The contribution of historical and ongoing practices at Martinac to
the metals contamination in the sediments 1s unknown. Sandblasting activities
and the use of antifouling paints are likely sources of contamination.
7.234
-------
CITY WATERWAY
American Plating (Puget Sound PI ating)--American Plating is located
at the head of City Waterway, where sediments are contaminated with metals.
Metals concentration in nearshore sediments in the vicinity of American
Plating were similar to those in offshore sediments near the head of the
waterway. Although American Plating may be contributing to the overall
contamination, it does not appear to be a major contributor. This electroplater
has been located at the upper end of City Waterway since 1975. Other electro-
platers (Puget Sound Plating and Seymour Electroplating) have occupied
the same property since 1955. Prior to 1978, the company was permitted
to discharge process wastes to City Waterway. WDOE files indicate numerous
permit violations. Subsequent to 1978, American Plating was connected
to the Tacoma Sewer Utility lines, and no longer had a permitted discharge
to the waterway. Plating wastes have been spilled at least 10 times since
1979, as documented in WDOE files. There have been two recent spills of
zinc-contaminated wastes. On October 6, 1981, an unknown volume of waste
containing 4 mg/L zinc was spilled on the property (WDOE files). On December
6, 1984, the company reported a spill of unknown volume of zinc-contaminated
effluent to the waterway. No copper waste spills have been documented
on American Plating property, although copper plating is performed at the
facility.
7.6.8.4 Summary and Recommendations--
Copper and zinc showed similar gradients of contamination in City
Waterway sediments, decreasing 1n concentration from the head to the moutn
of the waterway. Concentrations in Wheeler-Osgood Waterway were also elevated.
Contamination gradients suggest a source near the head, a source about
5,000 ft from the waterway mouth, and a possible source 1n Wheeler-Osgood.
Core data indicate that historical sediment accumulations of at least zinc
were greater than current accumulations.
The major current and historical sources of copper and zinc to the
waterway are the Nalley Valley and south Tacoma drains at the head of the
waterway. These two drains contribute over 80 percent of the quantified
copper and zinc loading to City Waterway. The relative inputs to the storm
drains from street runoff versus potential unpermitted industrial discharges
cannot be estimated.
The 15th Street and Wheel er-Osgood drains represent ongoing sources
of metals to C1tv Waterway. The 15th Street drain contributes 10 percent
of the quantified copper loading to the waterway and 8 percent of the zinc
loading. The Wheeler-Osgood drain contributes 2 percent of quantified
copper loading and 6 percent of the quantified zinc loading.
Martlnac Shipbuilding 1s probably a significant historical and ongoing
localized source to the waterway. Loading cannot be estimated from this
source, and the total amount of material discharged 1s unknown.
American Plating has a history of chronic spillage of plating wastes
to the upper waterway. However, available data Indicate that American
Plating is not presently a major source of copper and zinc to the waterway.
7.235
-------
CITY WATERWAY
A drainage basin study should be conducted to determine the major
sources of copper and zinc to the storm drains entering City Waterway.
This should include an attempt to identify unpermitted industrial or municipal
connections. Even if industrial sources can be identified and eliminated,
urban runoff is expected to remain a major source of both copper and zinc.
Reducing the metals input from runoff will require minimizing the amount
of particulate material discharged via the storm drains. Alternative techniques
to accomplish this goal are discussed in Section 7.6.9.5. If loadings
of copper and zinc from the Nalley Valley and south Tacoma drains can be
significantly reduced, a measureable improvement in sediment quality in
City Waterway can be expected over time. It is not possible to estimate
the rate of improvement because of the lack of data on sediment transport
and deposition within the waterway.
Continued monitoring and enforcement action at American Plating are
recommended. Activities at Martinac Shipbuilding should be investigated
to determine their contribution of contaminants to the waterway. Sources
of zinc and copper to Wheeler-Osgood Waterway should be investigated.
7.6.9 Lead
7.6.9.1 Spatial Distribution--
Lead concentrations (dry weight) in City Waterway surficial sediments
decreased steadily from the head to the mouth of the waterway. This is
apparent in Figure 7.6.21, which presents data from the Tetra Tech 1984
survey and from all available historical studies. The gradient of contamination
evident in this figure indicates that the major source of lead is located
at the head of the waterway and that a possible source exists in Wheel er-
Osgood Waterway. No other major sources along the length of the waterway
are apparent. Normalization of lead concentrations to percent fine-grained
material did not reveal other trends.
The vertical contamination gradient 1n sediments from Station CI-60
at the head of the waterway (Figure 7.6.22) indicates that lead input to
City Waterway sediments has steadily increased. The Station CI-60 core
showed a concentration of 48 mg/kg 1n the lowest horizon (1.3-1.52 m).
Above that, concentrations ranged from about 470 mg/kg in the 0.9 to 1.3-m
horizon to 1,040 mg/kg in the 0.1 to 0.3-m horizon. Elsewhere in the waterway
concentrations were more uniform throughout the core.
7.6.9.2 Loading Estimates-
Lead loading data are available from 10 storm drains discharging to
City Waterway (Table 7.6.8). In two other drains (one sample each), lead
was not detected at 1 ug/L. These data should be evaluated and used with
care, since most values are based on only two or three sampling events.
The exception 1s the Nalley Valley drain (CN-237) for which there were
seven sampling events. The Nalley Valley drain (CN-237) and south Tacoma
drain (CS-237) contributed 87 percent of the quantified lead input to the
7.236
-------
Segment:
900 ¦
800 ¦
rt
i
700 ¦
\
I
600 ¦
L
L
500 •
I
I
! 400 •
i 300 ¦
)
200
i
! 100
0

1
f
1
~
1
1
1
o «

1
1
©

1
1
1
1
o n

1
I

1
1
1
1
1
1
|
o
~
~

1
1
1
1
P
•
~ ~

1
1
t
1
1
© n

1
(

F' u Ra

o ^
i

0
p
9 °
~
~
~ !

o
i

D °
i
i
i

~
i

4 6
(Thousands)
Ft. from mouth of waterway
8
O Tttr* Itch Investigation • Quint1t»ted value
0 Other Investigations - Quantltated value
Figure 7.6.21
SURFICIAL SEDIMENT CONCENTRATIONS OF
LEAD IN CITY WATERWAY
Concentrations on a dry weight basis
7.237
-------
Concentration (mg/Kg-dry weight)
100 1000
10,000
i i
i i
¦

i I
Effects 1 !
AET | j
i i

i
i
i
I* Toxicity
j AET
i
1
i

m
1 j
! i

Figure 7.6.22
CONCENTRATION OF LEAD WITH DEPTH IN THE SEDIMENT
AT STATION CI-60, 605 NEAR THE HEAD OF CITY WATERWAY
7.238
-------
Table 7.6.8
LEAD: SUMMARY OF LOADINGS FROM DISCHARGES TO THE CITY WATERWAY
Drain #
Drain Name
Flow (MGD)
(Avg and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1) Loading
(Avg and Range) (lbs/day)
(1 of Observations) (Avg and Range)
CI-225
36" Concrete Storwdrain
under 11th St. Bridge
0.051
(0.032-0.07)
(n«2)
9/7/83
6
(n«l)
0.03
CI-230
15th St. Stormdraln,
48" Concrete Pipe
0.17
(0.14-0.22)
(n»3)
4/28/82-11/21/83
230
(3.5-650)
(n«3)
0.33
(0.005-0.92)
C J-234
24" Wood Box Outfall
at S. 21st Street
0.034
(0.03-0.037)
(n-2)
9/7/83-11/21/83
23
(9-37)
(n«2)
0.0065
(0.0023-0.010)
CI-243
21" Steel Pipe Storadraln
from RR Yard
0.37
(0.21-0.52)
(n«2)
9/7/83-11/21/83
5.5
(1-10)
(n-2)
0.017
(0.0031-0.031)
CI-245
18" Concrete Pipe Stora-
draln from RR Yard
0.070
(0.05-0.09)
(n*2)
9/7/83-11/21/83
1.0
(n-2)
0.00058
CI-248
IB" Concrete Pipe, B50 ft
S of 15th Street
0.020
(0.01-0.03)
(n«2)
9/7/83-11/21/83
3.5
(2-5)
(n-2)
0.00058
(0.00033-0.00083)
CI-703
Concrete Pipe Drain at
Harmon's Furniture
0.075
(0.06-0.09)
(n-2)
9/7/83
2
(n«l)
0.0013
CN-237
Nalley Valley Drain
3.6
11.2-10.66)
(n-8)
7/2B/81-4/17/B4
62
(3-360)
(n»7)
1.9
(0.09-11)
CS-237
South Tacoma Drain
4.8
(2.58-10.98)
(n>4)
2/16/82-9/7/83
33
(7-59)
(n-2)
1.3
(0.28-2.36)
CW-254
30" Steel Storadraln
E. End of Hheeler-Osgood
Waterway
0.29
(0.13-0.63)
(n«4)
7/28/81-11/7/83
40
(18-80)
(n-5)
0.097
(0.019-0.19)
NOTE: Lead has been analyzed for, but not detected In, the following drains: CI-Z08U) and CI-244(1). The number
In parentheses represents nufcer of analyses. Detection Units are 1 ug/1.
7.239
-------
CITY WATERWAY
waterway, providing 1.9 and 1.3 lb/day of lead, respectively. The 15th
Street drain and the drain at the head of Wheeler-Osgood Waterway contributed
substantially less lead (0.33 and 0.097 lb/day, respectively). Hi is may
be explained by the more limited drainage areas of the latter two storm
drains.
7.6.9.3 Source Identification--
Storm Drains--The spatial gradient of lead contamination and the docunented
discharge of lead through the Nalley Valley and South Tacoma storm drains
implicates these drains as the major sources of lead to City Waterway.
These drains serve a large portion of the city of Tacoma, as illustrated
in Figure 7.6.20. Particulate lead entering the waterway through these
storm drains probably results largely from automobile emissions in the
1-5 corridor and on residential streets.
Lead from automobile exhaust occurs in two basic forms: small particulate
material (0.1-0.5 um), which remains airborne for large distances, and
large particulate material (10-20 um), which is deposited within a few
meters of the emission point onto the roadway, adjacent shoulders, or off-road
areas (Pitt et al. 1981). While concentrations may vary dramatically,
lead is consistently detected in urban stormwater runoff. Its concentration
range resembles that of zinc and exceeds those of copper and chromium by
an order of magnitude (Galvin and Moore 1982). Although no effort has
been made to quantify lead released through automobile emissions in the
Tacoma area (Nolan, J., personal communication), the 1-5 corridor through
Tacoma is expected to have lead concentrations similar to those of 1-5
through Seattle [80-3,775 ug/L in highway runoff at two sites along 1-5
in Seattle, Chu1 et al. (1981)]. The increase in automobile traffic in
Tacoma over the years may help explain the steady Increase 1n lead concen-
trations in the CI-60 sediment core of the head of City Waterway.
Other Sources--The Tacoma Spur coal gasification site 1s located apprax-
Imately 1,000 ft southwest of the head of City Waterway. Hart-Crowser
and Associates (1984) studied soil and groundwater conditions at this site.
The maximum concentrations of lead measured during this study were 37.2
mg/kg 1n soil and 660 ug/L 1n groundwater. Possible sources of this contam-
ination other than the coal gasification by-products Include a coal- and
wood-fired generating station, petroleum product storage tanks, and an
abandoned gas station (Hart-Crowser and Associates 1984). These sources
are located near the head of City Waterway. Groundwater contamination
was attributed to the abandoned gas station, which provides a chronic input
of lead to City Waterway via groundwater. This source is realtlvely insig-
nificant compared to the amount of lead input via stormwater runoff.
Other potential sources of lead 1n sediments of City Waterway Include
spills of leaded fuels at the railroad yards and the petroleum bulk storage
yards near the mouth of the waterway. The magnitude of these inputs cannot
be quantified, but are not expected to be the large since waterway sediments
did not show elevated lead concentrations in these areas.
7.240
-------
CITY WATERWAY
Analyses by Norton and Johnson (1984) of lead in sediments offshore
of American Plating showed concentrations ranging from 737 to 810 mg/kg.
The concentrations were similar to those at the Tetra Tech 1984 station
at the head of the waterway (CI-11). The proximity of American Plating
to the 96-in storm drains does not permit adequate distinction between
lead inputs from the drains and from American Plating. However, WDOE files
give no indication that this company, or its predecessor, Puaet Sound Plating,
ever used lead in their processes. Thus, American Plating is not expected
to have contributed lead contamination in the waterway.
7.6.9.4 Summary and Recommend at ion-
Lead contamination in sediments in City Waterway decreased markedly
from the head to the mouth of the waterway, indicating a source near the
head of the waterway. This source is believed to be the Nalley Valley
and south Tacoma storm drains, both of which discharge at the head of the
waterway. Lead loading from these two drains alone has been calculated
at 3.2 lb/day, 87 percent of the total quantified loading of lead to the
waterway. The source of lead in these drains is suspected to be urban
runoff containing lead from automobile emissions and possible industrial
and municipal discharges to the drainage system. A possible source of
lead exists in Wheeler-Osgood Waterway.
Sources of lead into the storm drain systems should be investigated
and corrective actions to reduce discharges should be implemented where
feasible. Possible sources of lead to Wheel er-Osgood Waterway should be
Investigated.
7.6.10 Summary and Conclusions
The long history of Industrialization 1n City Waterway by numerous
small and moderate-size industries complicates source identification.
Historical waste handling practices are not well documented, and, in many
cases, present day waste production and disposal is not well quantified.
Known information regarding identified or potential sources of compounds
of concern to City Waterway are suimarized 1n Figure 7.6.23. Several Industries
and storm drains have been Identified as probable contributors of metals,
PAH, or total organic carbon (TOC) to City Waterway. Sources of dibenzofuran
are presumed to be the same as those for PAH. No sources were conclusively
Identified for PCBs, l,2-d1chlorobenzene, l,4-d1chlorobenzene, or 4-methyl-
phenol.
The Nalley Valley and south Tacoma drains are the major contributors
of many of the contaminants of concern to City Waterway. They are ongoing
sources of all metals of concern in the waterway, contributing 87, 88,
and 81 percent of the quantified loadings of lead, copper, and zinc, respec-
tively. One or both of these drains 1s also the major historical and poten-
tially ongoing source of organic material to the waterway. Finally, the
two drains are probably also a major ongoing source of PAH to City Waterway.
7.241
-------
•»* **eet petroleiw facujWs
Figure 7.6.23

-------
CITY WATERWAY
Discharge from the 15th Street drain contributes metals and PAH to
the waterway, but in much lower amounts than the two storm drains at the
head of the waterway. The 15th Street drainage basin is much smaller and
average flows are much lower.
Hygrade Foods and/or its predecessor, Carsten's Packing Company, appear
to be responsible for historical organic enrichment in Wheeler-Osgood Waterway.
Both were major dischargers of organic material. The potential of continuing
periodic discharges from Hygrade Foods 1s possible, as is natural decay
of accumulated organic debris in the anoxic basin. Storm drains to Wheeler-
Osgood Waterway are sources of copper, lead, and zinc. There may be other
sources of metals to the waterway as well. Possible sources of 4-methylphenol
to the Wheel er-Osgood Waterway are groundwater from the Tar Pits, and degrada-
tion of wood chip debris in the sediments.
Martinac Shipbuilding, near the juncture between City and Wheeler-
Osgood Waterways, is a probable source of copper and zinc to City Waterway.
Sandblasting and use of antifouling paints are suspected contributors.
North Pacific Plywood, Puget Sound Plywood, the Tar Pits, and the
Tacoma Spur (at 23rd and A Street) are all possible sources of 4-methyl-
phenol to City Waterway. Additionally, the Tacoma Spur and possibly the
Tar Pits site are potential ongoing sources of 4-methylphenol and LPAH
through groundwater. Discharges from North Pacific Plywood may have occurred
via groundwater or from spills of phenolic glues that entered the storm
sewer leading to the 15th Street drain. Glue wastes from Puget Sound Plywood
may be contributing to elevated sediment levels of 4-methylphenol seen
near the mouth of City Waterway.
The D Street petroleum facilities contribute LPAH to the waterway
via shallow groundwater seeping from the bank of the waterway. The problem
has been ongoing for 12 yr, 1f not longer. No relationship can be estab-
lished between the chemical contaminants In groundwater and the chemical
contaminants in the sediments (Johnson and Norton 1985). The D Street
petroleum facilities are not believed to be the source of HPAH seen in
the sediments at the mouth of the waterway, although the actual source
has not been definitively identified.
Investigations are necessary to determine the sources of the petroleum
products observed 1n the storm drains near West Coast Grocery and in the
vicinity of 15th Street. Potential sources Include several old gasoline
stations, a historical railroad roundhouse, and Chevron. A historical
source of PAH that will probably never be quantified is spills and bilge
pumping.
7.243
-------
RUSTON-PT. DEFIANCE SHORELINE
7.7 RUSTON-PT. DEFIANCE SHORELINE
7.7.1 Introduction
The Ruston-Pt. Defiance Shoreline study area extends along the south-
west shore of Commencement Bay from the Point Defiance Zoo and Aquarium
to the mouth of City Waterway. This area was the location of the original
Tacoma settlement in the late 1800s and the site of the Tacoma Mill, the
first lumber mill on Commencement Bay, which began cutting in 1869. Other
industries which had been located on the Ruston-Pt. Defiance Shoreline
include eight lumber companies, two grain elevator facilities, a lime company,
a boat building operation, a fuel company, a cold storage company, and
railroad freight warehouses (Ruckelshaus unpublished).
The Tacoma Smelter opened on the Ruston-Pt. Defiance Shoreline in
1889 as a lead smelter. It was modified for copper smelting about 1906
when it was bought by American Smelting and Refining Company (ASARCO).
Lead smelting was discontinued in 1911. Copper refining facilities were
built in 1913 and arsenic recovery systems were added in 1917 (Sims 1979).
Facilities for production of sulfuric acid and sulfur dioxide were added
in later years. Depressed metal prices led to closure of the metal refining
facilities at ASARCO in 1978. The copper smelter was closed in the spring
of 1985. Currently, only the arsenic trioxide plant is in operation; shutdown
was expected before the sunnier of 1985 (Pierce, R., personal communication).
Other facilities currently operating on the Ruston-Pt. Defiance Shoreline
are shown in Figure 7.7.1. They Include the Pt. Defiance Ferry Terminal
Slip, Tacoma Yacht Basin, City of Tacoma F1re Station No. 5 Pier, Continental
Grain Company, Tacoma Elevator Wharf, and Tacoma North Sewage Treatment
Plant (STP). Otherwise, much of the shoreline and area to the south is
residential housing and small commercial establishments.
The Ruston-Pt. Defiance Shoreline has had several modifications to
its waterfront as a result of dredge and fill operations. The peninsula
enclosing the Tacoma Yacht Basin was formed by copper smelting slag placed
under permits issued from 1917 to 1962. Slag was also used to build up
the shoreline on which much of the ASARCO plant is now located. Between
55,000 and 90,000 yd3 of the slag near the Tacoma Yacht Basin was removed
and replaced with riprap under a 1977 permit. Other permits have been
Issuea for fill operations to stabilize shoreline embankments. A summary
of the dreding projects 1s presented 1n Table 7.7.1.
Locations of known discharges to the Ruston-Pt. Defiance Shoreline
are shown in Figure 7.7.1. The only NPDES-permltted discharges are from
ASARCO (RS-003, RS-004, and RS-005) and Tacoma North STP (RS-022). ASARCO's
discharge permit Includes limits for pH, oil and grease, and flow volume.
The company has also been required to monitor arsenic, cadmium, copper,
lead, and zinc discharges. Although the smelter has closed, there 1s still
some discharge from these outfalTs, primarily site runoff and noncontact
cooling water (Pierce, R., personal communication). The Tacoma North STP
has discharge permit limits for biochemical oxygen demand, total suspended
7.244
-------
Point Defiance
Park
Point Defiance
Ferry Terminal
Yacht
Cldb
Merlcan Sneltlng
ft Refining Co
kl

Ticom North Sewage
Treatiwnt Plant
TacoM F1re
Station #5 Pier
v>v
m

£
s
1800 3600
.Continental Grain Co. »
' Tacoma Elevator Wharf
Figure 7.7.1
MAJOR INDUSTRIES AND DISCHARGES TO THE RUSTON SHORELINE
-------
TABLE 7.7.1. SUMMARY OF DREDGING PROJECTS,
RUSTON-PT. DEFIANCE SHORELINE
Year
Permitee
Quantity
(yd3)
Comments
1977
ASARCO
17,000
Slag fill
1980
Industrial Mineral Products
90,000
55,000 yd3 dredged
by 1980
1982
Crown Pacific Corporation
4,300
Dredge and fill
1983
ASARCO
850
Gravel fill
Unknown
Tacoma Metro Park District
Unknown

Reference: U.S. Army Corps of Engineers dredging permits, as compiled
by M. Ruckelshaus, WDOE.
7.246
-------
RUSTON-PT. DEFIANCE SHORELINE
solids, fecal coliform bacteria, and flow volume. Numerous storm drains
discharge from the Ruston-Pt. Defiance Shoreline. The largest ones are
a 60-in storm drain at Alder Street (RS-029), a 60-in storm drain 250 m
northwest of McCarver Street (RS-039), and a 48-in drain 225 m northwest
of McCarver Street (RS-040).
The locations of sediment chemistry sampling stations along Ruston-Pt.
Defiance Shoreline, shown in Figure 7.7.2 include those sampled as part
of the Superfund investigation, as well as all historical sampling sites.
Eleven contaminants or groups of contaminants were designated as preliminary
contaminants of concern on the Ruston-Pt. Defiance Shoreline. These contam-
inants and their respective areas of concern are
Organic Compounds Inorganic Substances
Aromatic hydrocarbons (Segments 1 and 2) Arsenic (Segments 1 and 2)
Dibenzofuran (Segment 1) Cadmium (Segment 2)
PCBs (Segment 2) Copper (Segments 1 and 2)
Phenols (Segment 1) Lead (Segments 1 and 2)
Chlorinated benzenes (Segment 1) Mercury (Segments 1 and 2)
Z1nc (Segment 2)
Station RS-13 was the only station in Segment 1 designated to be of
concern because of observed sediment toxicity or benthic effects. Biological
data were not available for Station RS-15, but it was later determined
to be a potential problem station because several chemical concentrations
exceeded AET when normalized to percent fine-grained material or organic
carbon content. No dry-weight concentrations exceeded AET at Station RS-
15 and no source evaluations were conducted in this area. A potential
problem area 1n Ruston-Pt. Defiance Shoreline Segment 3 was ultimately
defined on the basis of AET values. This area had not been designated
to be of preliminary concern and no source evaluations were conducted.
Arsenic, copper, lead, and mercury are listed as of preliminary concern
in Segment 1 (Station RS-13) and source evaluations were conducted for
them. It was later determined that concentrations of these contaminants
did not exceed AET at Station RS-13. Concentrations of all other chemicals
listed above as of preliminary concern were determined to exceed AET 1n
their respective areas. Other contaminants whose concentrations were ultimately
determined to exceed AET but were not subjected to source evaluations include
Substance Station Where AET (dry weight) Exceeded
Dichlorobenzenes RS-18
N-n1trosodiphenylamine RS-18, RS-24
Methyl phenols RS-13, RS-18
Phthalate esters RS-16
Dibenzofuran RS-16, RS-18, RS-21
Antimony RS-16, RS-17, RS-18,
RS-19, RS-21, RS-24
Nickel RS-17, RS-18, RS-21
7.247
-------
%
%

~ RS-22
1
~ RS-24
,RS-10 (HOAA)

<&
* &
*% Sediment
Core RS-62
~
s
f
*
f
Sedime
Sedlm
* N
!
JUrs-
15
J-3
J?
& jp-
~ RS-14/RS-0Z
*¦?>

%
&
.10
RS-22 (ROW)
X X^"13 (WOAA)
X RS-21 (HOW)
~
~ Tetra Tech
A EPA
X Other Agencies
1800 3000
FEET
i otner Aa<
~ WDOE, 191
184
METER8
AsP
S? SP> RS-13
(Segment 1
Station of Concern)
~ RS-04
IRS-12
Figure 7,7.2
SURFICIAL SEDIMENT STATIONS AND SEDIMENT CORE
LOCATIONS FROM ALL STUDIES ON THE RUSTON SHORELINE
7.248
-------
RUSTON-PT. DEFIANCE SHORELINE
Antimony and nickel concentrations normalized to percent fine-grained material
exceeded AET at most stations in Segment 2. These substances probably
derive from the same sources as the other metals in Segment 2. Concentrations
of several tentatively identified compounds were also determined to exceed
AET in either Segment 1 or 2 [i.e., 1-methyl(2-methylethyl)benzene, biphenyl,
dibenzothiophene, methylphenanthrenes, retene, and methylpyrenes]. These
substances are not discussed further, but likely derive from similar sources
as the PAH.
Average mass flux estimates were not calculated for any of the priority
contaminants along the Ruston-Pt. Defiance Shoreline because of major uncertain-
ties concerning the appropriate area of deposition required for the analysis.
In any case, spatial distributions clearly indicate the major sources of
contaminants in Segment 2. There are insufficient data with vJhich to determine
sources of contaminants for the hot spot around Station RS-13 in Segment 1.
7.7.2 Spatial Distribution
The distributions of contaminants of concern in surficial sediments
of the Ruston-Pt. Defiance Shoreline are shown 1n Figures 7.7.3-7.7.14.
All contaminants showed similar gradients, with highest concentrations
at Stations RS-17, 18, 21, and/or RS-13.
The metals, PAH, and dibenzofuran typically showed the highest concen-
trations normalized to dry weight, TOC, or percent fine-grained material
at Stations RS-17, 18, and 21. Concentrations of the contaminants in this
area were typically one to two orders of magnitude higher than those elsewhere
along the Ruston-Pt. Defiance Shoreline. Of the three stations adjacent
to the ASARCO shoreline (RS-17, 18, and 21), none had the highest concentrations
for all contaminants. Station RS-17 had the highest arsenic concentrations;
Station RS-18 had the highest cadmium, lead, mercury, and PAH concentrations;
and Station RS-21 had the highest copper and zinc concentrations.
PCB concentrations were elevated (>500 ug/kg) at several Tetra Tech
stations 1n Segment 2 (Including RS-16, 17, and 21) and at one station
in Segment 1 (NOAA station RS-13, a different site than the Tetra Tech
RS-13).
Elevated concentrations of PAH and dibenzofuran, normalized to both
dry weight and organic carbon, were found at Tetra Tech Station RS-13,
1n Segment 1. Lead, mercury, and zinc concentrations were also elevated
at Station RS-13.
The phenols and chlorinated benzenes were designated to be of concern
along the Ruston-Pt. Defiance Shoreline at Station RS-13. Within these
two contaminant groups, 2-methylphenol and 1,4-dlchlorobenzene showed the
most apparent increased concentrations at this station. The spatial distribu-
tions of these compounds are shown in Figures 7.7.12 and 7.7.13. Both
showed increased concentrations at Station RS-13, the site nearest the
7.249
-------
mg/kg dry weight
~6!
~700
19000
,~16
~ 25
1*00 3000
~ Tetra Tech
A EPA
X Other Agencies
~ UDOE. 1964
mt
METfM
~ Exceeds AET (see TabltM.l for AET values)
isoo
•oo
Figure 7.7.3
CONCENTRATIONS OF ARSENIC IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
7.250
-------
mg/kg dry weight
110
~ 16
,u0.1
0.22.
MtTtRS
•00
1*00
M
~ Tetr» Tech
A CPA
X Other Agencies
~ VDOE, 1984
^Exceeds AET (see Table 4.1 for AET values)
Figure 7.7.4
CONCENTRATIONS OF CADMIUM IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
u * undetected at concentration shown
7.251
-------
~87
mg/kg dry weight
~ 390*
xno
'~137
1400#
~ 2200#
P55
X 43
~ 99
1800 3600
Mirou
•00
1800
~ Tetr» 1«ch
A EPA
X Other Agencies
~ WDOE. 1984
^Exceeds AET (see Table 4.1 for AET values)
Figure 7.7.5
CONCENTRATIONS OF COPPER IN THE
SURFICIAl SEDIMENTS OF THE RUSTON SHORELINE
u « undetected at concentration shown
7.252
-------
mg/kg dry weight
~ 530
2700
160
X29
* 41 X209
|Q X46
116
1SOO MOO
¦ssa Fin
MCTCNS
900
~ Tetre Tech
A EPA
X Other Agencies
~ HOOE. 1984
#Exceeds AET (see Table 4.1 for AET values)
Figure 7.7.6
CONCENTRATIONS OF LEAD IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
7.253
-------
mg/kg dry weight
O0.41
.9*
J.4
.75
0.12
X0.1
tu0.02
1800 3600
0.016
* * 0.39
*00
taoo
10.14
~ Tetr* Tech
A EPA
X Other Agencies
~ WOE, 1984
IfrExceeds AET (see Table 4.1 for AET values)
Figure 7.7.7
CONCENTRATIONS OF MERCURY IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
u * undetected at concentration shown
7.254
-------
~ 200
mg/kg dry.weight
~ 1600
X140
180
COO
'~140
~ 900*
000*
'3301
100
~ 72
1600 3600
IP X91
•00
ieoo
~ Tetr* Tech
A CPA
X Other Agencies
~ WDOE, 1984
* Exceeds AET (see Table 4.1 for AET values)
Figure 7.7.8
CONCENTRATIONS OF ZINC IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
7.255
-------
vg/kg dry weight
~ L 210
L 110
6210
D 4110
~ LI300
1900
6400*
~ 200
X L75
~ Z1100
360
2000
.2200
~Exceeds AET (see Table 4.2 for AET values)
~ L14
mg/kg TOC
O 126
182
200
150
~ L220
,~ 56

3600
A*
No organic carbon normalized AET exceeded
(see Table 4.6 for AET values)
MfTMt
too
~ Tetra Tech
4 WDOE, 1984
X Other Agcnclei
Figure 7.7.9
CONCENTRATIONS OF LOW MOLECULAR WEIGHT PAH IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
L s At least one of the components of the group was undetected,
sum included the detection limit.
Z = Data corrected for blank.
7.256
-------
o 177
pg/kg dry weight
~ 900
X 360
4.000
980
~ 3100
1800
131001
~ L420
X 150
12301
4500
7100
UtExceeds AET (see Table 4.2 for AET values)
mg/kg TOC
O 110
L91
460
350
~ 540
250
L120
V 190 88
x x
\aq*37
1500*
isoo moo
^^3 '
-------
~ u5
mg/kg dry weight
/
-/V-
~Exceeds AET (see Table 4.2 for AET values)
t
ui.e
1*00 3600
O Tetra Tech
mg/kg fines
\D1.4

~ Exceeds AET (see Table 4.9 for AET values)
Figure 7.7.11
CONCENTRATIONS tiF DIBENZOFURAN IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
u = undetected at concentration shown
7.258
-------
~ Exceeds AET (see Table 4.2 for AET values)
4* Exceeds AET (see Table 4.6 for AET values)
~ Tetra Tech
Figure 7.7.12
CONCENTRATIONS OF 2-METHYL PHENOL IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
u = undetected at concentration shown
7.259
-------
~ uS
yg/kg dry weight
D us
BO. 5
~lO
¦250
40
~L14
1230
~Exceeds benthlc effects and toxicity AET of 120 yg/kg DW
mg/kg TOC
~ul.8
BO.4
2.3
ul.8
2.0
2.8
>0.2
lul.4
1800 3600
<0.8
1.0
•00
0 Exceeds AET of 3 ag/kg TOC
(benthlc effects AET >16 but not established)
1800
~ Tctra Tech
CONCENTRATIONS OF 1,4-DICHLOROBENZENE IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
u = undetected at concentration shown
B » blank contribution greater than observed value
z - data corrected for blank
7.260
-------
yg/kg dry weight
~ 6
XO.l
'~4
DlO
550$
*33
~Exceeds AET (see Table 4.2 for AET values)
mg/kg TOC
O 2
2.3
0 .f
2.8
ul.9
0.2
5.5 7.8
1*00 9600
Firr
MCTKM
BOO
1800
0.6
0.6
~ Tetra Tech
A EPA
X Other Agencies
~ Exceeds AET (see Table 4.6 for AET values)
Figure 7.7.14
CONCENTRATIONS OF PCBs IN THE
SURFICIAL SEDIMENTS OF THE RUSTON SHORELINE
u * undetected at concentration shown
7.261
-------
RUSTON-PT. DEFIANCE SHORELINE
RS-039 and RS-040 outfalls. A second area of elevated 1,4-dichlorobenzene
concentrations was detected at Station RS-18 near the RS-004 outfall.
Sediment cores were not taken in Segment 1. Therefore, assessment
of historical trends in contaminant input was not possible. Three sediment
core samples were taken in Segment 2, one each near the three major outfalls
in this segment. The concentrations with depth of selected priority contami-
nants are shown in Tables 7.7.2 and 7.7.3.
Similar vertical patterns of PAH and dibenzofuran contamination occurred
in all three cores. Concentrations in the upper horizon were consistently
higher than those in the lower horizons. Different vertical patterns of
PCB and metals contamination occurred in the three cores. PCB concentrations
increased with depth at Station RS-60, decreased with depth at Station
RS-61, and were the same in both horizons at Station RS-62. Metals concentra-
tions at Station RS-60 remained constant or decreased slightly with depth.
At Station RS-61, there was a consistent increase in concentration in Horizon
1 (0-0.038 m) followed by an approximate 1.5- to 5-fold decrease in concentra-
tion below that depth. A subsurface increase in concentration occurred
in Horizon 4 (0.15-0.41 m) for most compounds, although zinc showed a subsurface
maximuti in Horizon 5 (0.41-0.44 m). There was little consistency in compound
concentrations at Station RS-62. Arsenic, zinc, and cadmium concentrations
were higher in the upper horizon (0-0.051 m), while mercury, copper, and
lead concentrations were higher in the lower horizon (0.051-0.23 m).
Each of the three sediment cores was located near one of three major
outfalls. The differences among cores in vertical gradients of metals
and PCB concentrations probably reflect differential input of these contam-
inants from the various outfalls. Discharge RS-005 historically was a
deep water outfall (exact dates of operation were not confirmed), which
may explain the lower metals concentrations in the lower horizon of sediment
core RS-62. The differences in vertical gradients among cores also suggest
that deposition of airborne particulates 1n the bay is not the major source
of the observed metals and PCB contamination. If this were the case, similar
vertical patterns of contamination would be expected in each core.
7.7.3 Loading Estimates
Loading estimates were available for five outfalls on the Ruston-Pt. Defi-
ance Shoreline. These outfalls, for which flows have been measured, Include
RS-003, RS-004, and RS-005 (the ASARC0 outfalls); RS-022 (the Tacoma North
STP outfall); and RS-040 (a 48-in city storm drain near McCarver Street).
Loading estimates for RS-003, RS-004, and RS-005 do not Include the discharge
monitoring data from ASARCO's NPDES permit, only sampling data from industrial
survey inspections.
7.7.3.1 Organic Compounds--
Analyses for organic compounds 1n this area are limited. Available
data are shown in Table 7.7.4.
7.262
-------
Table 7.7.2
CONCENTRATIONS OF ORGANIC COMPOUNDS WITH DEPTH IN THE SEDIMENT
Contamlnant
Low Molecular High Molecular Total
Weight PAH Weight PAH Dlbenzofuran PCBs
Sediment Core RS-60, BOl
Horizon 1 (0-0.038 m) 6,000a 19,800a 410 760
Horizon 2 (0.038-0.127 m) 4,160 17,280a 140 1,500
Sediment Core RS-61, BOl
Horizon 1 (0-0.038 m) 10,260a 22,420a 890a 2,400
Horizon 2 (0.038-0.11 m) 4,620 21,420a 330 540
Horizon 3 (0.11-0.15 m) 980 4,000 61 360
Horizon 4 (0.15-0.41 m) 2,500 12,750® 200 410
Horizon 5 (0.41-0.44 m) 710 L 2,790 64 U 140
Sediment Core RS-62, BOl
Horizon 1 (0-0.051 m) 4,140 16,380a 200 340
Horizon 2 (0.051-0.23 m) 1,900 7,220 110 340
Concentrations as ug/kg dry weight
U ¦ undetected at concentration shown
L ¦ less than
a Value exceeds toxicity or benthic AET.
-------
Table 7.7.3
CONCENTRATIONS OF ARSENIC AND METALS WITH DEPTH IN THE SEDIMENT
Sediment Core RS-60, BOl
Horizon 1 (0-0.038 m)
Horizon 2 (0.038-0.127 m)
Sediment Core RS-61, BOl
Horizon 1 (0-0.038 m)
Horizon 2 (0.038-0.11 m)
Horizon 3 (0.11-0.15 m)
Horizon 4 (0.15-0.41 m)
Horizon 5 (0.41-0.44 m)
Sediment Core RS-62, BOl
Horizon 1 (0-0.051 m)
Horizon 2 (0.051-0.23 m)
Contaminant3
Arsenic Mercury Copper Lead Zinc Cadmium
6,200 6.2 14,200 4,280 2,520 77
4,400 5 14,600 3,450 2,780 56
20,000 6.2
2,850 4.2
2,350 0.6
4,300 8.5
2,800 2.8
29,500 13
5,800 21
35,800 10,400
9,110 2,040
4,720 2,180
12,700 3,860
5,170 3,070
4,110 3,300
21,200 3,640
9, J60 282
4,060 36
7,010 24
5,580 56
12,900 31
2,950 231
2,470 60
Concentrations as mg/kg dry weight.
a Concentrations of all contaminants
listed exceed toxicity and benthic
AET in every horizon shown.
-------
Table 7.7.4
ORGANIC COMPOUNDS: SUMMARY OF LOADINGS FROM
DISCHARGES ALONG THE RUSTON SHORELINE
Drain I
Drain Name
Flow (MGD)
(Avg. and Range)
(I of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(f of Observations)
Loading (lbs/day)
(Avg. and Range)
LOU MOLECULAR WEIGHT
RS-022
Tacoma North Sewage
Outfall
4.8
(n»l)
6/30/79-9/14/81
3.9
(2.1-5)
(n-3)
On two occasions, LPAH have been analyzed for but not detected In RS-040. Detection limits was 10 ug/1.
RS-022 Included acenaphthene, naphthalene, fluorene, phenanthrene, and anthracene.
1.16
(0.084-0.20)
Compounds detected In
H16H MOLECULAR HEIGHT PAH
RS-022 Tacoma North Sewage 4.8 6/30/79-9/14/81 13 0.52
Outfall — (12-15) (0.48-0.60)
(n-1) (n-2)
On two occasions, HPAH have been analyzed for but not detected In RS-040. Detection limits ranged from 10 to 20 ug/1.
Compounds detected in RS-022 Included chrysene, benzo(k)fluoranthene, benzo(b)fluoranthene, pyrene, fluorantehene, and
d1benzo(a,h)anthracene.
CHLORINATED BENZENES
RS-022 Tacoma North Sewage 4.8 6/30/79-9/14/81 19 0.76
Outfall — (2-35) (0.080-1.4)
(n-1) (n-2)
On two occasions, chlorinated benzenes have been analyzed for but not detected 1n RS-040. Detection limits were 10 ug/1.
Compounds detected 1n RS-022 included 1,2-dtchlorobenzene, 1,3-dlchlorobenzene, and hexachlorobenzene.
TOTAL PHENOLS
RS-022 Tacoma North Sewage 4.8 6/30/79-9/14/81 L 14 L 0.56
Outfall — (L 10-18) (0.40-0.72)
(n-1) (n-2)
On two occasions, phenols have been analyzed for but not detected 1n RS-040. Detection limits were from 30 to 60 ug/1.
Compounds detected In RS-022 were phenol and pentachlorophenol.
7.265
-------
RUSTON-PT. DEFIANCE SHORELINE
7.7.3.2 Inorganic Compounds--
Loading estimates of metals to the waters off the Ruston-Pt. Defiance
Shoreline are shown in Tables 7.7.5-7.7.9. Highest concentrations of these
contaminants were found at the ASARCO south outfall (RS-005). Loadings
from this outfall were an order of magnitude higher than those from any
other outfall. The next highest loadings were estimated for the ASARCO
middle outfall (RS-004). Arsenic, copper, and zinc were the three major
contaminants in discharges from the ASARCO plant. Arsenic loadings were
approximately three times those of copper and four times those of zinc.
Because the ASARCO outfall discharges have not been analyzed for mercury,
corresponding loading data were not available.
7.7.4 Source Identification
Spatial distribution of contamination in the surficial sediments of
the Ruston-Pt. Defiance Shoreline indicates two areas of elevated concentra-
tions for the contaminants of concern. The first is located in Segment
2 adjacent to the property owned by ASARCO. Metals, PAH, and PCBs have
been designated as contaminants of concern and all showed elevated concentra-
tions within this area. A second site of elevated contaminant concentrations
is at Station RS-13 in Segment 1. Sediments from this station had elevated
concentrations of PAH, dibenzofuran, 2-methylphenol, and 1,4-dichlorobenzene
relative to those from other stations in Segment 1. Spatial gradients
of contamination are insufficient to support conclusive identification
of major sources of metals in Segment 1. The two areas of elevated contaminant
concentrations are discussed individually below.
7.7.4.1 Ruston-Pt. Defiance Shoreline Segment 2 - ASARC0--
The ASARCO facility was built as a lead smelter in 1889 and reconstruc-
ted as a copper smelter 1n 1906 when it was bought by the American Smelting
and Refining Company. Over the years, copper smelting and refining, nickel
extraction, and arsenic production occurred. The economics of production
determined which activities took place. The ASARCO plant was one of the
few facilities in the world that smelt ore highly contaminated with materials
such as sulfur and arsenic. Much of this ore originated in the Philippines
and Central America. The plant operated on consignment, mixing and smelting
batches of material for specific customers. With changing markets in copper
and other metals, production at the plant has steadily decreased over the
past 5 yr.
In January, 1985, production of metallic arsenic operations at the
ASARCO plant were discontinued. Only arsenic trioxide is produced at the
present time. Prior to January, 1985, production activities Included copper
smelting, sulfur dioxide and sulfuric acid production, and elemental arsenic
and arsenic trioxide production. For economic reasons, copper refining
and nickel extraction had ceased some years earlier. Arsenic trioxide
is currently produced from the residual arsenic concentrates on the plant
site. It used to be produced as a by-product of the copper smelting process.
Arsenic dust was recovered from the roasters, furnace, and converters,
7.266
-------
Table 7.7.5
ARSENIC: SUMMARY OF LOADINGS FROM DISCHARGES ALONG THE RUSTON SHORELINE

Drain 1
Drain Name
Flow (MGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(I of Observations)
Loading (lbs/day)
(Avg. and Range)

RS-003
ASARCO North Outfall
0.4B
(0.32-0.63)
(n-2)
11/18/75-9/15/82
78
(8-150)
(n-5)
0.31
(0.032-0.60)
RS-004
ASARCO Middle Outfall
1.2
(1.0-1.4)
(n-2)
11/18/75-9/15/82
7.800
(38-18,500)
(n«6)
78
(0.38-185)
RS-005
ASARCO South Outfall
3.4
(1.5-4.3)
(n-3)
11/18/75-9/15/82
14.000
(260-80,000)
(n-8)
400
(7.4-2,300)
RS-022
Tacoma North Sewage
Outfall
4.8
(n-1)
6/30/79-4/28/82
39
(6.5-110)
(n-4)
1.6
(0.26-4.4)
RS-040
48-inch Concrete Pipe
0.91
(0.64-1.2)
(n-2)
9/14/81-4/28/82
9
(5-13)
(n-2)
0.068
(0.038-0.10)
NOTE: Arsenic has been detected In RS-020 (5 ug/1) and In RS-070 (20-3,800 ug/1); however, no flow data are available froo
which to calculate loadings.
7.267
-------
Table 7.7.6
CADMIUM: SUMMARY OF LOADINGS FROM DISCHARGES ALONG THE RUSTON SHORELINE
Drain f
Drain Name
Flow (MGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/day)
(Avg. and Range)
RS-003
ASARCO North Outfall
0.48
(0.32-0.63)
(n-2)
2/24/81-9/15/82
L 3
(1-L 5)
(n-2)
I 0.012
(0.0040-L 0.020)
RS-004
ASARCO Middle Outfall
1.2
(1.0-1.4)
(n-2)
11/16/7 5-9/15/82
92
(50-170)
(n-4)
0.92
(0.50-1.7)
RS-005
ASARCO South Outfall
3.4
(1.5-4.3)
(n*3)
11/18/75-9/15/82
360
(30-1.700)
(n-7)
10
(0.85-48)
RS-022
Tacona North Sewage
Outfall
4.8
(n-1)
6/30/79-4/28/82
(0.87-5)
(n-3)
0.092
(0.035-0.20)
RS-040
48-1nch Concrete Pipe
0.91
(0.64-1.2)
(n-2)
4/28/82
2
(n-1)
0.015
NOTE: Cadmium has been detected In RS-020 (30 ug/1) and In RS-070 (32 ug/1); however, no flow data are available from which to
calculate loadings.
7.268
-------
Table 7.7.7
COPPER AND MERCURY: SUMMARY OF LOADINGS FROM
DISCHARGES ALONG THE RUSTON SHORELINE
Drain #
Drain Name
Flow (HGD)
(Avg. and Range)
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (1bs/d*y)
(Avg. and Range)
COPPER
RS-003
ASARCO North Outfall
0.48
(0.32-0.63)
(n-2)
11/18/75-9/15/82
290
(40-700)
(n-5)
1.2
(0.16-2.8)
RS-004
ASARCO Middle Outfall
1.2
(1.0-1.4)
(n-2)
11/18/75-9/15/82
3,300
(60-6,700)
(n-5)
33
(0.6-67)
RS-005
ASARCO South Outfall
3.4
(1.5-4.3)
(n-3)
11/18/75-9/15/82
4,200
(150-15,500)
(n-8)
120
(4.3-440)
RS-022
Tacoma North Sewage
Outfall
4.8
(n-1)
6/30/79-4/28/82
52
(32-65)
(n-4)
2.1
(1.3-2.6)
RS-040
48-Inch Concrete Pipe
0.91
(0.64-1.2)
(n-2)
4/28/82
10
(n-1)
0.076
NOTE: Copper was analyzed for but not detected 1n RS-020. Detection limit ms 50 ug/1. Copper has been found 1n RS-070 on
four occasions (160-380 ug/1); however, no flow data are available from which to calculate loading.

MERCURY

RS-022
Tacoma North Sewage
Outfall
4.8
£i)
8/20/79-4/28/82
1.4
(0.36-3.5)
(n-3)
0.056
(0.014-0.14)
RS-040
48-1 nch Concrete Pipe
0.91
(0.64-1.2)
(n-2)
9/14/81-4/28/82
0.35
(0.26-0.43)
(n-2)
0.0027
(0.0020-0.0033)
7.269
-------
Table 7.7.8
LEAD: SUMMARY OF LOADINGS FROM DISCHARGES ALONG THE RUSTON SHORELINE
Drain f
Drain Name
Flow (MGD)
(Avg. and Range)
(I of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (?bs/day)
(Avg. and Range)

RS-003
ASARCO North Outfall
0.48
(0.32-0.63)
(n-2)
2/24/81
71
(n-1)
0.28
RS-004
ASARCO Middle Outfall
1.2
(1.0-1.4)
(n-2)
11/18/75-2/24/81
360
(200-760)
(n-2)
3.6
(2.0-7.6)
RS-005
ASARCO South Outfall
3.4
(1.5-4.3)
(n«3)
11/18/75-9/15/82
360
(34-2,300)
(n-8)
10
(0.96-65)
RS-022
Tacoma North Sewage
Outfall
4.8
(n»l)
6/30/79-9/14/81
3.0
(1.4-6)
(n-3)
0.12
(0.056-0.24)
NOTE: Lead has been analyzed for but not detected In RS-040. Detection limits ranged from 2 to 20 ug/1. Lead has been
detected 1n RS-020 (200 ug/1) and RS-070 (29-400 ug/1); however, no flow data are available from which to calculate
loadings.
7.270
-------
Table 7.7.9
ZINC: SUMMARY OF LOADINGS FROM DISCHARGES ALONG THE RUSTON SHORELINE
Drain f
Drain Name
Flow (MGD)
(Avg. and Range]
(# of Observations)
Period
of Observations
for Contaminant
Concentrations
Concen-
tration (ug/1)
(Avg. and Range)
(# of Observations)
Loading (lbs/da>)
(Avg. and Range)

RS-003
ASARCO North Outfall
0.48
(0.32-0.63)
(n-2)
11/18/75-9/15/82
49
(10-160)
(n-4)
0.20
(0.04-0.64)
RS-004
ASARCO Middle Outfall
1.2
(1.0-1.4)
(n-2)
11/18/75-9/15/82
2.600
(2,000-4.500)
(n-4)
26
(20-45)
RS-005
ASARCO South Outfall
3.4
(1.5-4.3)
(n-3)
11/18/75-9/15/82
3,400
(430-14,000)
(n«7)
96
(12-400)
RS-022
Tacoma North Sewage
Out faJ J
4.8
(n-1)
6/30/79-4/28/82
150
(20-380)
(n-4)
6.0
(0.80-15)
RS-040
48-1 nch Concrete Pipe
0.91
(0.64-1.2)
(n-2)
9/14/81-4/28/82
39
(20-57)
(n-2)
0.30
(0.15-0.43)
NOTE: Zinc has been detected 1n ftS-020 (60 ug/1) and in RS-070 (50-430 ug/1); however, no flow data are available from which
to calculate loadings.
U.271
-------
RUSTON-PT. DEFIANCE SHORELINE
and then sent to the arsenic recovery plant where it was volatilized, settled,
and condensed. The production of elemental arsenic and arsenic trioxide
occurred separately. Arsenic trioxide was heated and recondensed in elemental
form as a solid and shipped out (U.S. EPA 1983b).
Copper ore arrived at the plant by ship. Off-loading occurred at
the southern dock. Ore was crushed either prior to shipment or at the
plant. It was stored for smelting in the fine ore building. Most waste
materials and sludges generated in process were also put into the fine
ore building and eventually resmelted.
Specific historical practices that have contributed most heavily to
the observed contaminants in Commencement Bay cannot be determined because
of the age of the facility and the relatively short (i.e., 20-yr) history
of regulated emissions and discharges. The main stack and the main smelting
operations date back to the turn of the century. The refinery buildings
were added in the early 1920s and the sulfur dioxide plant was added in
the mid-1970s. WDOE inspections have consistently failed to trace drainage
lines from various buildings to their ultimate discharge point. Dye testing
has been tried numerous times and consultations with plant managers and
employees have had limited success.
As discussed in Section 7.7.3, most metals of concern (except mercury
and nickel) have been measured in ASARCO discharges. Although the effluent
has not been analyzed for organic compounds of concern, at least some of
them could be associated with spills from the ASARCO facility. Each contaminant
of concern is discussed below with regard to its known or potential presence
in ASARCO effluent, atmospheric emissions, surface runoff, or groundwater.
Metals (Arsenic, Copper, Cadmium, Lead, Mercury, Zinc)--Numerous sources
of metals at the ASARCO facility could have released pollutants along the
Ruston-Pt. Defiance Shoreline. Among them are the three NPDES-permitted
ASARCO outfalls, which discharge 8.4 M6D of site runoff and noncontact
cooling water to Commencement Bay. Prior to 1976, when discharge of contact
cooling water ceased, contact and noncontact cooling waters were mixed
and discharged through the outfalls (Springer 1975). The ASARCO outfalls
also discharge stormwater runoff, which 1s contaminated with metals from
stack fallout and from fugitive dust emissions from the various process
buildings (U.S. EPA 1983b; Springer 1976; Pierce, R.t personal communi-
cation). The outfalls also carry runoff originating as groundwater seeps
1n the area of the plant stack (Hart-Crowser and Associates 1976).
Typically, the south outfall (RS-005) contains the highest concen-
trations of metals. The flow from this discharge 1s aproxlmately 3-4 MGD
and 1s composed of saltwater noncontact cooling water from the acid plant,
springs, surface runoff from ASARCO property, and miscellaneous freshwater
input from cooling water use. This discharge enters a dispersion pond
made from slag, from which the water percolates into the bay. Chronic
problems of overflow and direct discharge to the bay have been noted 1n
this area (Heffner 1981). This outfall pond is known to flood at high
tide, with direct mixing and overflow.
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RUSTON-PT. DEFIANCE SHORELINE
The middle outfall (RS-004) drains the primary smelting areas, arsenic
storage areas, and the copper anode pond where contact cooling waters were
recirculated. It also serves as a surface stormwater runoff ditch. The
flow from RS-004 is approximately 1-2 MGD.
The north outfall (RS-003), with the smallest of the three flows (approxi-
mately I MGO), drains the old refinery areas and the laboratory. Water
from the foul water system, which drains the area of the arsenic kitchens,
may be discharged indirectly through this outfall.
A 54-in city of Ruston storm drain (RS-002) located to the north of
the ASARCO property discharges runoff from the oil tank storage areas and
powerhouses. It is unknown if this drain serves other areas of the plant
or if cross-connections exist with the north outfall system. Sampling
data are not available for this drain (Pierce, R., personal communication).
The drain may flow at 1-2 MGD, much of it from the ASARCO property.
ASARCO's NPDES permit established limits for flow, pH, and oil and
grease. ASARCO was required to monitor metals in their discharges although
no limits were established. Because of the problems associated with tidal
flooding, particularly in the south outfall, these data may not be accurate.
However, the discharges generally improved with time as the company installed
recirculation devices and as smelting production decreased (Pierce, R.,
personal communication). With shutdown of smelting activities in March,
1985, the only remaining discharge from the outfalls is runoff and cooling
water from the foul water system.
Metals may migrate from the facility via groundwater. In January
and March, 1985, WDOE collected groundwater samples from wells on ASARCO
property. Metals analyses indicated that concentrations of arsenic, cadmiun.
and lead were above the maximum contaminant levels as defined by National
Interim Primary Drinking Water Regulations. Concentrations of organic
contaminants were at acceptable levels.
The metals in groundwater may have originated from ASARCO slag. Most
of the plant property west of Ruston Way is composed of slag. In the early
years of the plant's history, molten slag was dumped directly into seawater.
Later, dikes were constructed and molten slag was dumped behind them.
Many of the plant's facilities now stand on land created by these activities.
Although slag depth has not been measured, 1t is known to extend 10-12 m
below sea level at the seaward edge of the property (Cloud 1979). Portions
of the slag are known to have cracks and gas pockets, allowing water to
move through these materials (Cloud 1979). Although no data are available
regarding groundwater contamination on the ASARCO property, release of
metals via this route could be significant, particularly because of the
tidally Induced flushing of the slag fill. In addition, there have been
chronic, low-volume discharges of acidic wastewaters (pH 1-2) to the ground
as recently as 1982 (Pierce and Anderson 1982a). Acidic conditions would
promote leaching of metals from the slag.
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RUSTON-PT. DEFIANCE SHORELINE
Another major route for release of metals is air emissions from the
main stack at ASARCO and from dust process emissions. In a permit granted
by the Puget Sound Air Pollution Control Agency (PSAPCA), limitations were
established for total particulates, sulfur oxides, and arsenic emissions.
In addition, the facility was required to monitor and report lead and mercury
emissions to PSAPCA on a monthly basis (Anderson, J., personal communication).
Process emissions declined with production declines. There has been little
or no decrease in emissions due to installation of new process controls
in the last few years (Anderson, J., personal communication). Direct dust
fallout from the stack and fugitive emissions from the plant property have
not been studied well. It has been estimated (U.S. EPA 1983b) that about
34 lb/h of arsenic may be released via fugitive arsenic process dust emissions,
with most of the arsenic coming from process of gases in the converter
operation of the plant.
Crecelius et al. (1975) indicated that the arsenic-to-antimony ratio
in ASARCO smelter stack dust is about 10 to 1, while the ratio in slag
is about 1 to 1. Sediments collected in the vicinity of ASARCO and throughout
the nearshore/tideflats area during the Superfund project typically showed
arsenic-to-antimony ratios well in excess of 20 to 1, making it impossible
to discriminate contamination by atmospheric sources from that of other
sources using this technique.
Metals are released to Commencement Bay from the ASARCO facility via
atmospheric emissions, outfall discharges, surface water runoff, and ground-
water. Available data are inadequate to establish which of these routes
has been the greatest contributor to the observed contamination. Changes
in metal input as a result of the plant's closure cannot be determined
at this time. Because soils on plant property are contaminated, discharge
of metals via runoff will continue. Release of contaminants via groundwater
will also continue.
Polycyclic Aromatic Hydrocarbons--Heavy residual fuel oils, such as
Bunker C, are used at the ASARCO facility to fuel the furnaces, roasters,
and converters. The bunker oils are brought 1n by ship, off-loaded at
the north dock, and stored in large tanks on the north end of the property.
These tanks are bermed, but the bottom of the storage area is not sealed.
A 1982 inspection by WDOE noted oil within the diked area (Pierce and Anderson
1982b). Spills of Bunker C oil from all three outfalls have been reported
in WDOE files, and past spills have coated the si age trench of the middle
outfall with Bunker C oil (Randt 1976). Spills have also occurred during
off-loading of tankers and transfer of oils to bulk storage tanks.
Another source of HPAH to this area of Commencement Bay is combustion
of Bunker C oil and subsequent release via stack emissions. Fluoranthene/1n-
deno(c,d)pyrene ratios (f/1) at Stations RS-17 and RS-03 are high (38 to
>150), possibly indicating a specific combustion source such as ore smelting
(see Section 7.2.3.3). However, the lack of a consistently high f/1 ratio
at all stations around ASARCO suggests that smelting combustion products
are not the sole source of HPAH.
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RUSTON-PT. DEFIANCE SHORELINE
Lighter fuels, such as gasoline and diesel, are used in small equipment
pumps and vehicles at various places on the property. Light fuels are
stored near the central dock. According to ASARCO's July, 1983 SPCC plan,
three gasoline tanks and one diesel tank are buried underground. Other
light fuel storage tanks are present on the property above ground. An
oil pimping station is located in the central dock area, as well. An oil/water
separator was installed along the middle outfall line in the late 1970s.
Lighter fuels have spilled to the ground and drained to each of the
outfalls over the years. ASARCO's NPDES permit allows no more than 15 mg/L
of oil and grease and no visible sheen. A number of WDOE inspections have
noted sheen in the outfalls and oil stains on the ground. Samples from
Station RS-18, off the middle outfall (RS-004), showed the highest surficial
sediment contamination of both LPAH and HPAH on a dry-weight basis. This
is consistent with known spillage of fuels in the central portion of the
plant, which would eventually reach the middle outfall and nearby bay
sediments. HPAH concentrations were also elevated off the north outfall
and north dock, consistent with spillage of Bunker C oil during off-loading.
PCBs--There are at least three potential PCB sources on the ASARCO
property: two powerhouses and a utility substation. The Cottrell powerhouse
supplies power to large electrostatic precipitators used in final processing
of copper, arsenic, and sulfur oxides. Additional transformers are located
north of this powerhouse in the drainage area served by RS-002. As of
1982, the company was slowly changing to non-PCB-contain1ng transformers.
A WDOE inspection on May 11, 1982 (Pierce and Anderson 1982b) noted the
presence of oil stains on the floors 1n the Cottrell powerhouse. If spills
were to occur from this powerhouse, it is likely (although not proven)
that liquids would drain to the anode pond and subsequently through the
middle outfall (RS-004).
A second Cottrell powerhouse, located on the southwestern portion
of the property which supplies power to the liquid sulfur dioxide facility.
This facility was completed in 1974 (ASARCO undated). PCB concentrations
1n existing and past transformers in this powerhouse, if any, are not known.
Spills from this facility would drain into the bay through the south outfall
(RS-005).
A Tacoma City Light substation is located at the northern end of the
plant property. It 1s unknown whether this substation contains any transformers
with PCB oils, but it 1s likely that this was the case historically. Spills
from this facility would drain to the north outfall (RS-003) or to the
60-in city of Tacoma storm drain (RS-002), and subsequently to Commencement
Bay.
Sediment core data do not reveal whether PCB contamination 1s historical
or ongoing, since the vertical pattern of contamination 1s different 1n
each core. Recent contaminant Input appeared greater than historical input
1n only one core (Station RS-61 off the north outfall). It 1s unknown
whether any of the transformers on the ASARCO property or at the Tacoma
City Light substation still contain PCB oils. The ultimate disposition
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RUSTON-PT. DEFIANCE SHORELINE
of the ASARCO transformers if arid when the facility closes entirely is
also unknown.
7.7.4.2 Ruston-Pt. Defiance Shoreline Segment 1 - Station RS-13--
Samples from Station RS-13 in Segment 1 were found to contain aromatic
hydrocarbons, dibenzofuran, 2-methylphenol, and 1,4-dichlorobenzene concentra-
tions that were 1.4-5.5 times greater (dry-weight basis) than those at
other stations in Segment 1. This would suggest the presence of at least
one source in the vicinity of Station RS-13.
A breakdown product of lignin, 2-methylphenol is commonly found in
pulp mill effluents. The chlorination of monochlorobenzene produces 1,4-
dichlorobenzene, which is used as an Insecticide and air deodorant (U.S. EPA
1980c). The PAH are components of petroleum products and thus are ubiquitous
in a heavily developed area such as Tacoma.
The Ruston-Pt. Defiance Shoreline in the vicinity of Station RS-13
is occupied by several fish markets and restaurants (e.g., Johnny's Ocean
Fish, Carrs Landing, Charlie's Fish Bar). None of these establishments
is likely to be major sources of these compounds. However, an industry
no longer in the area may have been the source. Hie only industries known
to have occupied the area are the Tacoma Mill, which operated from 1892
through about 1920, Tacoma Boatbuilding, and Aero Jet. No other information
is available on historical Industries In the area, and there are no sediment
core samples that would permit an assessment of historical patterns of
contaminant input.
An alternative source for the contamination observed in samples from
Station RS-13 is the city storm sewer system. Rogers et al. (1983) reported
two major discharges 1n the vicinity of Station RS-13: a 60-in concrete
pipe (RS-039) and a 48-in concrete pipe (RS-040), both located about 150
m west of Station RS-13. The RS-039 outfall is no longer used; all effluent
is diverted to RS-040. The drainage area served by RS-039/040 1s approximately
500 ha 1n size and includes the University of Puget Sound and a residential/
light commercial area of Tacoma.
The RS-040 outfall does not appear to be a likely ongoing source for
the contamination observed at Station RS-13 for several reasons. First,
2-methylphenol and 1,4-dichlorobenzene would not be expected 1n a typical
effluent originating as runoff from a residential area. Second, the RS-040
effluent has been analyzed on two occasions for these compounds, and detectable
concentrations were not reported (see Section 7.7.3). Finally, drain RS-029
serves an adjacent area of comparable size to that served by RS-040. Although
both drainage areas are of similar composition (principally residential,
with some small commercial establishments) only sediments in the vicinity
of the RS-040 outfall showed elevated concentrations of aromatic hydrocarbons,
2-methylphenol, and 1,4-d1chlorohenzene. Comparable contamination was
not observed at Stations RS-14 and RS-02 near the RS-029 outfall.
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RUSTON-PT. DEFIANCE SHORELINE
Drains RS-039/040 may have been a source of the contaminants of concern
in the past. Prior to the early 1960s, the RS-039 outfall discharged domestic
sanitary sewage as well as runoff. The compounds of concern may have been
introduced to the bay at that time and are now present in surficial sediments
as a result of recent sediment disturbance. However, there have been no
dredging activities in this area in recent years.
7.7.5 Summary and Recommendations
No sources can be definitively identified for the contaminants of
concern at Station RS-13 in Segment 1. The spatial distributions of the
inorganic contaminants of concern generally showed little evidence of a
major source within this segment. Metals concentrations in samples from
Station RS-13 were typically two orders of magnitude less than those in
neighboring Segment 2. Neither nearby properties nor drains appear to
be likely ongoing sources for the organic contaminants present in samples
from Station RS-13. However, it is possible that historical industries
or past discharges (pre-1960 to 1962) from drain RS-039 were the source
of the contaminants. Further attempts at source identification would require
additional sampling to confirm the contamination now evident only on the
basis of a single sample; to determine if there is a spatial gradient of
contamination to help identify the source(s); and to determine whether
contamination is ongoing, recent, or historical.
Sediment contamination in Segment 2 can be attributed to the ASARCO
property, with the possible exception of PCBs. The firm is a documented
major source of metals, with the plant's three NPDES-permitted outfalls
alone contributing 780 lb/day of metals to Commencement Bay. Many documented
releases of fuels have contributed to the PAH contamination now observed
in sediments of the Ruston-Pt. Defiance Shoreline. Transformers containing
PCBs have been used on the ASARCO property. While there have been no documented
spills from these transformers, the spatial gradient of PCB contamination
in the bay sediments suggests that releases have occurred. Tacoma City
Light maintains an electrical substation near the ASARCO property. Past
spills from this facility could also be responsible for the observed contam-
ination of bay sediments, particularly near the ASARCO north outfall.
Although ASARCO is the major source of contaminants in Segment 2,
for most of the contaminants it 1s not possible to conclude that the major
input has occurred through single route. Contaminants may migrate from
the ASARCO property into the bay through several routes:
• Outfalls - Four outfalls serve the ASARCO property, three
of which are NPDES-permitted. Their effluents originate
from a variety of sources, Including stormwater runoff,
groundwater seepage, noncontact cooling water, contact cooling
water (pre-1976), and spills. The three discharges have
been sampled are major soyrces of metals. These outfalls
have also carried spilled petroleum products to the bay,
contributing to the PAH contamination. The high PCB concentra-
tions (>500 ug/kg) along the ASARCO shoreline suggest that
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RUSTON-PT. DEFIANCE SHORELINE
spills in any or all of three transformer yards have entered
the bay through these outfalls.
• Groundwater - Much of the ASARCO property has been created
by the dtmping of molten slag into Commencement Bay. Movement
of groundwater through this slag, promoted by tidal action,
may be a significant source of metals to the bay. Chronic
discharges of acidic wastewater may have enhanced leaching
of metals from the slag. The historical practice of spreading
molten slag on the ground surface and irrigating it to promote
cooling may also have contributed to metals contamination
via groundwater.
• Atmospheric Emissions - Atmospheric deposition from the
stack emissions may contribute to stormwater runoff and/or
groundwater contamination.
A decrease in contaminant release can be expected with the recent
closure of the copper smelting operations at ASARCO, particularly in atmospheric
emissions. However, groundwater and discharge of storm water and/or cooling
water through the four outfalls can be expected to continue introducing
contaminants to the bay for many years to come.
A comprehensive air, water, and sediment quality monitoring program
is recommended to determine the effect of reduction in plant operations
on contaminant release and appropriate remedial actions. This investigation
should include components to assess fugitive dust emissions, soil quality,
geohydrology, outfall effluent characterization, and receiving environment
quality. Until this investigation is complete, it will be Impossible to
determine appropriate source control activities and their effectiveness
in reducing contamination in Bay.
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8. RECOMMENDATIONS OF AREAS AND SOURCES
FOR POTENTIAL REMEDIAL ACTIONS
8.1 INTRODUCTION
The final prioritization of problem areas for potential remedial actions
is presented in this section. Recommendations of areas and sources for
these remedial actions are based on evaluations of:
• The environmental hazard indicated by the problem area con-
tamination, toxicity, and biological effects
• The spatial extent of each problem area
• The confidence that sources of potential problem chemicals
in each problem #rea have been identified.
A prioritization of problem areas and problem chemicals was made in
Section 6. Eight problem areas were given a high priority for source
evaluation, four problem areas were given a second priority for evaluation,
and nine problem areas were not included for priority source evaluation.
The spatial extent of each problem area was also defined 1n Section 6,
but was not considered in the development of recommendations of problem
areas for source Identification. In this section, the relative spatial
extent of each problem area 1s considered, along with the magnitude of
contamination, toxicity, and biological effects. For example, large areas
with a high degree of environmental hazard are ranked higher than isolated
hot spots posing a similar hazard. Source evaluations for each problem
area are also rated according to the level of confidence that the problem
sources have been identified. Thus, the highest ranking problem area for
potential remedial action 1s large, poses a substantial environmental hazard,
and has wel 1-characterized sources. In this ranking method, a small "hot
spot" exhibiting substantial effects that have been traced confidently
to a contaminant source may be ranked at the same, or even higher, priority
than a much larger problem area with unknown sources. To allocate resources
efficiently, "hot spots" with known sources would be recommended for potential
remedial action before the larger area with unknown sources.
Potential remedial actions Include source control and/or sediment
remedial action (see Tetra Tech 1984a). The feasibility of such actions
1s considered 1n a separate report for Task 6 of the Commencement Bay Superfund
Remedial Investigation.
A final prioritization of Commencement Bay problem areas is presented
1n Table 8.1. Scores for each problem area 1n three categories (environmental
significance, spatial extent, and confidence of source identification)
were summed to estimate the relative priority for potential remedial action.
Environmental significance was scored from 1 to 4 according to the magnitude
of observed contamination, toxicity, and biological effects. The eight
highest-priority areas identified in Section 6.4 were given a score of 4
8.1
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TABLE &.1 FJHAL RANKING OF PROBLEM AREAS
Segment

Confidence

Containing
Environmental
Spatial
of Source
Total

Problem Area*
Significance
Extent
Identification
Score

RS52
4
4
4
12

SPS1
4
3
4
11

C1S1
4
3
4
11

HYS5
4
3
4
11

srsi
4
4
3
11

HYS1
4
4
3
11

HYS2
4
2
4
10

CIS2
4
I
3
8

MDS1
3
3
2
8

RSS3
1
3
4
ft

CIS3
3
2
2
7

BYS4
3
2
I
€

RSSla (RS-13)
3
1
1
5

BLS2
2
1
\
4

MSI
2
1
\
4

RSSlb (RS-1S)
1
1
I
3

HYS3
I
1
1
3

BLSI
1
1
1
3

HYS6
1
1
1
3

BLS3
1
1
1
3

BLS4
1
1
1
3

• Problem areas (fid not always encompass an entire segment. Problem areas
In the segments Indicated are listed order of their totirt score for
environmental significance, spatial extent, and confidence of source Identi-
fication.
11 Identification of potential remedial technologies was conducted for prob-
lem areas with a total score greater than or equal to 7.
8 a
-------
for environmental significance. The four second-priority sites (Section
6.4) were given a score of 3, and the two third-priority sites (plus Milwaukee
Waterway) were given a score of 2. All remaining lower-priority problem
areas were given scores of 1.
The spatial extent (surface sediments only) of each problem area was
estimated by planimetry. Problem area boundaries were established by the
location of current and historical stations where chemical concentrations
exceeded AET. Historical stations for which only amphipod bioassay data
were available were also used to set problem area boundaries when high
toxicity (>50 percent mortality) was indicated. No interpolation of chemical
concentrations was attempted between stations because of the often patchy
distribution of problem sediments. However, when no data were available
for nearshore subtidal and intertidal sediments, the problem areas were
assumed to extend to the shore. Scores were assigned on the basis of size
of each problem area as follows:
• >50 acres score = 4
• 30-50 acres score = 3
• 10-30 acres score = 2
t <10 acres score = 1.
The confidence of source identification was scored according to the
following qualitative criteria:
• Ongoing sources were well-identified by spatial patterns
of contamination (and effects), and by chemical characteristics
that matched those of the receiving water environment;
score=4. Or, contamination was clearly established as
historical, although sources may not have been well-identified;
score=4
• Potential sources were identified, but their relative contri-
butions compared with historical deposits were not clear;
score=3
• Adjacent sources were suggested by land use or drainage
patterns, but spatial patterns of contamination were ambiguous;
score=2
• Source unidentified; score=l.
All problem areas with clearly Identified sources (i.e., score=4)
exhibited major environmental effects. The exception was the problem area
within Segment RSS3 on the Ruston-Pt. Defiance Shoreline, where the source
of metals contamination is believed to be ASARC0 slag or ores In the sediments.
No benthic data directly comparable to those 1n other areas (I.e., 0.06-m2
grab) were collected from this problert area because of sampling difficulties.
However, qualitative evaluation of replicate 0.1-m2 grab samples indicated
a general similarity to Carr Inlet reference conditions. The differences
in numbers of species and abundances of the major taxonomic groups were
8.3
-------
not large, and probably reflected natural differences in benthic community
structure between the Segment RSS3 site and Carr Inlet. Therefore, major
impacts to benthic communities did not appear to be occurring in the potential
problem area. Based on this qualitative analysis, the score for environmental
significance was reduced from 2 to 1 (Table 8.1). This problem area is
still recommended for evaluation of potential remedial action.
All problem areas in Table 8.1 with a total score <6 have a low priority
for evaluation of potential remedial action. These latter problem areas
had largely unidentified sources and were not extensive. Potential hot
spots in Segments HYS4 (Hylebos Waterway) and RSS1 (Station RS-13; Ruston-Pt.
Defiance Shoreline) are included in this group. Ship scour or some un-
identified dredging activity could have resulted in the multiple significant
benthic depressions observed at a single station (HY-37) in the Segment
HYS4 hot spot. Further characterization of potential sources is required
for the Station RS-13 hot spot within Segment RSS1. Further source identifica-
tion of problem chemicals summarized in Table 6.14 (see Section 6.5) is
recommended for each of these low priority problem areas before the feasibility
of any potential remedial action is evaluated.
Recommendations for the remaining problem areas with scores >7 in
Table 8.1 are presented below.
8.2 RECOMMENDATIONS FOR POTENTIAL REMEDIAL ACTION
Potential remedial actions include source control and sediment actions
such as removal, capping, or in situ treatment. All problem areas discussed
below have ongoing, potentially ongoing, or unknown sources of problem
chemicals. Remedial actions with respect to the contaminated sediments
is recommended for all areas only after the sources have been Identified
and effectively controlled.
8.2.1 Hylebos Waterway
Hylebos Problem Area 1 (in Segment HYS1)--
Potential sources of HPAH, arsenic, copper, lead, and zinc were identified
for the problem area 1n Segment HYS1 of Hylebos Waterway. Source control
measures are recommended to reduce HPAH discharge from Kaiser Ditch. Source
control evaluation is also recommended to reduce metals discharge (especially
arsenic and zinc) from unpaved log sort-yards (Wasser Winter, Cascade Timber
yard #2, Dunlap Towing, Louisiana Pacific), and from Hylebos Creek (B&L
Landfill and Fife Ditch).
Hylebos Problem Area 2 (1n Segment HYS2)--
PCBs were the highest priority chemicals found 1n the problem area
defined within Hylebos Segment HYS2. Exposure of historical accumulations
of PCBs (and other chemicals, I.e., HCBD) by dredging was Identified as
the most probable source of this contamination. There was little evidence
of an ongoing source of PCBs 1n this area. A PCB source reconnaissance
is recommended prior to evaluation of sediment remedial action. Potential
source control must also be evaluated for other problem chemicals discussed
below that have significant ongoing sources in this problem area. The
8.4
-------
extent of subsurface PCB contamination was not well-characterized, but
likely extends over a broad area. This problem should be considered when
planning dredging projects in Hylebos Waterway.
Elevated HPAH concentrations were found in subtidal sediments of the
problem area in Segment HYS2 near the boundary between Segments HYS1 and
HYS2. These sediments do not appear to be within the dredged area discussed
for PCBs. The HPAH contamination is likely an extension of the contamination
found in the problem area within Segment HYS1. As discussed previously,
source control evaluation for HPAH has been recommended for the Kaiser
Ditch, the major HPAH source to Hylebos Waterway.
Pennwalt Chemical Corporation was identified as an ongoing source
of chlorinated ethenes, chlorinated butadienes, arsenic, copper, lead,
and zinc to intertidal sediments of the Segment HYS2 problem area. Tetrachloro-
ethene is also elevated in some of the subtidal sediments. Source control
evaluation is recommended for these chemicals in the main plant outfall,
surface drains, groundwater seeps, and groundwater in shallow ana intermediate
aquifers.
Hylebos Problem Area 3 (in Segment HYS5)--
Source control evaluation for chlorinated compounds, including chlorinated
ethenes and chlorinated butadienes, from Occidental Chemical Co. is recom-
mended. Although chlorinated butadienes (with the exception of HCBD) did
not exceed toxicity or benthic AET (Section 6), source control for these
substances is still recommended for the Occidental main outfall based on
their extreme concentrations in this area. Very high concentrations of
chlorinated ethenes in this area were restricted to the immediate vicinity
of the Occidental Chemical Co. docks. Because of the localized nature
of this contamination, clear response gradients could not be established.
However, because of the magnitude of chlorinated ethene contamination,
these substances warrant a high priority for source control. The source
of PCB contamination in this area was not established. A PCB reconnaissance
in this area is recommended. PCB contamination in this area should be
considered when dredging is planned.
8.2.2 Sitcum Waterway
Ore unloading operations at the Port of Tacoma docks are a potential
source of metals contamination to the north shore of the waterway. Although
the contribution of this source to overall sediment metals contamination
cannot be established with available data, it is recommended that evaluations
be conducted on possible control technologies for minimizing release of
ore into the waterway.
Three storm drains are also major contributors of metals to Sitcum
Waterway. Source identification within the drainage areas of these storm
drains is necessary before source controls can be Implemented.
8.2.3 St. Paul Waterway
The main outfall from the Champion International pulp mill located
at the mouth of St. Paul Waterway, is an ongoing source of alkylated phenols
8.5
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(or their precursors), methoxyphenols, copper, organic enrichment, and
chloroform. Source control evaluation for alkylated phenols (or their
precursors) is recommended at Champion International pulp mill. Source
control for copper and chloroform is also recomnended because these contaminants
were measured at elevated concentrations in plant effluent or, in the case
of copper, exceeded applicable water quality criteria.
8.2.4 Middle Waterway
Ship repair operations were identified as potential sources of mercury
and copper in Middle Waterway. No definite sources of pentachlorophenol,
dichlorobenzenes, and PAH have been identified. Evaluation of source control
at the ship repair operations is recommended. Source investigations for
pentachlorophenol, dichlorobenzenes, and PAH are recommended before evaluating
source controls.
8.2.5 City Waterway
City Problem Area 1 (in Segment CIS1)--
The south Tacoma and Nalley Valley drains at the head of City Waterway
are the largest ongoing sources of metals (especially lead) and organic
material. The specific sources of metals and organic matter within these
drainage areas have not been identified. Therefore, source investigations
are recommended within these drainage areas. Source control alternatives
should be evaluated following identification of specific sources. Source
investigations and source control evaluations should also be conducted
for the 15th Street drain, which also contributes metals and PAH to the
waterway. Source control evaluation is recommended for Martinac Shipbuilding,
which is a probable source of copper and zinc to City Waterway. The wood
products industries, the Tar Pits site, and the 23rd and A Street coal
gasification site are possible sources of 4-methylphenol to City Waterway.
The contributions of 4-methylphenol from these sources should be Investigated.
City Problem Area 2 (1n Segment CIS2)--
Ongoing sources of the contaminants of concern in Wheeler-Osgood Waterway
could not be identified. Source investigations are therefore recommended
for 4-methylphenol, 1,2-dichlorobenzene, organic material, lead, and zinc.
Source investigations should Include evaluation of specific sources of
these contaminants within the drainage area served by CW-254. The potential
for groundwater transport of 4-methylphenol from the Tar Pits site also
requires further investigation.
City Problem Area 3 (in Segment CIS3)--
Sources of the problem contaminants in City Waterway Segment 3, including
LPAH and HPAH, could not be Identified with existing information. Therefore,
remedial action for this problem area is not recommended until contaminant
sources and transport mechanisms have been established. Further source
investigation is recommended for PAH.
8.6
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8.2.6 Ruston-Pt. Defiance Shoreline
The ASARCO facility was identified as the source of metals (including
high-priority mercury and arsenic) and PAH to the adjacent problem area.
Although ASARCO is the major source of contaminants to the problem area,
for most of the contaminants it is difficult to determine if the major
loading has occurred through any one route (i.e., process effluent, surface
water runoff, groundwater). Because the facility has closed recently,
a characterization and source control evaluation of the residual discharge
of contaminants from site runoff and groundwater is recommended. A recon-
naissance survey is recommended to determine possible sources of PCBs to
this problem area.
8.3 GENERAL RECOMMENDATIONS
There were several PCB hot spots in the project area where PCBs concen-
trations exceeded apparent effects thresholds. In addition, general PCB
contamination within the waterways is sufficient to be the apparent cause
of elevated PCBs in fish muscle, fish liver, and crab muscle tissue. PCBs
are the chemicals that are responsible for the highest predicted risk to
human health from fish consumption. The sources of PCBs are unknown.
A general reconnaissance survey of the area for PCB sources with appropriate
followup where warranted is recommended. Other chemicals for which general
reconnaissance surveys are recommended include aromatic hydrocarbons and
dibenzofuran.
8.7
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9.0 OVERVIEW OF CONTAMINATION AND BIOLOGICAL EFFECTS
IN COMMENCEMENT BAY
The Commencement Bay Nearshore/Tideflats Remedial Investigation included
a comprehensive assessment of sediment contamination and associated biological
effects. Results of this assessment were used to identify and prioritize
problem areas. An overview of these conditions in Commencement Bay is
provided in this section.
During this and previous studies, several hundred chemicals have been
tentatively identified in Commencement Bay sediment samples. Routine analyses
have been conducted for about 150 chemical variables. Chemicals detected
in over two-thirds of the surface sediments analyzed 1n the Superfund study
included phenol, 4-methyl phenol, PAH, 1,4-dichlorobenzene, PCBs, dibenzofuran,
and most U.S. EPA priority pollutant metals. Most of these chemicals had
already been reported in many areas of Commencement Bay. Chemicals detected
only rarely or not at all in the present study included pesticides, most
organonitrogen compounds, most chloro- and nltrophenols, halogenated ethers,
2,3,7,8-dibenzodioxin (never detected), selenium, and thallium. High concen-
trations of some of the pesticides in this group had been found 1n past
studies, but the findings had not been confirmed by mass spectroscopy.
Sediment contamination throughout the Commencement Bay study area
is variable both in concentration and composition. The highest PAH concen-
trations were found near the head of Hylebos Waterway. Benzo(a)pyrene
was found at over 1,000 times reference conditions at one Hylebos Waterway
station. In this study and in others, Hylebos Waterway sediments contained
a complex mixture of chlorinated compounds, many of which were unidentified.
Tri- and tetrachlorinated butadienes were found at well over 1,000 times
reference conditions near the mouth of the waterway. Other chemicals measured
at over 1,000 times reference concentrations were 4-methyl phenol and 2-methoxy-
phenol (guaiacol) 1n sediments adjacent to the main outfall of the Champion
International pulp and paper mill 1n St. Paul Waterway, and four metals
(antimony, arsenic, copper, and mercury) 1n sediments adjacent to the main
outfalls of the now closed ASARC0 copper smelter on the Ruston-Pt. Defiance
Shoreline. With some exceptions, concentrations of most chemicals measured
in the current investigation of subtidal sediments were comparable to or
higher than those in subtidal and intertidal sediments collected in previous
studies. Chlorinated ethene concentrations 1n Intertidal sediments from
Hylebos Waterway were higher 1n other studies than those in subtidal sediments
in the present study. Metal concentrations In sediments near drains at
the head of Sitcum Waterway were also higher 1n other studies.
In the present study, Blair and Milwaukee Waterways contained the
least contaminated subtidal sediments. Additional sampling was not conducted
in the Puyallup River, but historical sediment concentrations were low.
The most extreme contamination in the remaining areas was typically located
in small areas near point source discharges. Pronounced gradients in chemical
concentrations were observed 1n several waterways (e.g., Hylebos, St. Paul,
and City Waterways) and along the Ruston-Pt. Defiance Shoreline. Concentra-
9.1
-------
tions of contaminants in sediments collected well outside of Hylebos and
Blair Waterways were low, approaching reference conditions in most cases.
For most substances, the range of concentrations was greater in subsurface
sediments than in surface sediments. The depth of penetration in the sediments
was often limited by textural characteristics. Concentrations approaching
reference area conditions for all chemicals were reached at the bottom
of only some cores. Many chemicals present at elevated concentration at
depth in cores were still below apparent effect thresholds for toxicity
and benthic effects. Consistently low concentrations of chemicals were
reached at the bottom of all cores collected in a special drilling program
in Blair Waterway.
Studies of benthic macroinvertebrate assemblages and laboratory bioassays
of sediments were used as site-specific Indicators of biological effects
and toxicity in Commencement Bay. These studies demonstrated that areas
of high toxicity and effects on benthos were generally isolated near known
pollutant sources. The most severe effects were observed at single sampling
stations near two industrial facilities: Champion International pulp mil I
and the ASARCO smelter. In these areas of extreme adverse effects, very
few animals lived in the sediments or survived a 10-day laboratory exposure
to the sediments. These areas were also characterized by very high sediment
contamination in which concentrations of several chemicals were over 1,000
times higher than reference concentrations. In these two areas, there
was noticeable improvement in benthic conditions at the next closest transect
stations (250-400 ft away) , indicating that the areas of maximum effects
were of limited spatial extent. Biological conditions varied considerably
from station to station in the waterways. For example, in Hylebos Waterway,
areas of high toxicity and altered benthic communities were interspersed
among areas of low toxicity and benthic effects. Some waterways displayed
well-defined areas of high toxicity and benthic effects (e.g., Hylebos
and City Waterways) and others displayed little evidence of such effects
(e.g., Milwaukee and Middle Waterways).
In general, the waterway sediments supported higher abundances of
benthic macroinvertebrates than were found 1n Carr Inlet or along the Ruston-
Pt. Defiance Shoreline. The waterway sediments supported fewer species
than other areas sampled, indicating possible generalized effects from
contamination, sediment disturbance, or presence of fine-grained sediments.
Typical benthic assemblages in the waterways were dominated by polychaete
worms and small clams. These organisms are important food items for many
bottom-feeding fishes.
Demersal fish assemblages 1n the waterways were dominated by flatfishes
such as English sole. F1sh assemblages 1n the waterways were over twice
as abundant as those 1n Carr Inlet. These fishes may be attracted by the
abundant food resources 1n the waterways or by the increased habitat complexity
1n the harbor environment. B»gl1sh sole 1n several waterways had significantly
elevated prevalences of one or more liver lesions. The highest overall
lesion prevalence was measured 1n Middle Waterway, where 40 percent of
English sole sampled had one or more serious lesions. The causes of these
lesions are unknown, but the lesions are similar to those Induced 1n laboratory
animals exposed to toxic chemicals. The effects of these lesions on the
fish are also unknown. In this study, however, fish with serious liver
9.2
-------
lesions did not exhibit reduced condition (as expressed by weight at a
given length) when compared to fish without lesions.
Although many chemicals were highly elevated in Commencement Bay sediments,
relatively few were detected in the tissues of English sole and crabs.
The only metals that were accumulated above reference levels were copper
in English sole and lead and mercury in crabs. PCBs were the most consistently
detected organic compounds and were measured at concentrations about 10
times reference levels in Hylebos and City Waterways. In the heavily fished
Pt. Defiance area, concentrations of PCBs in English sole were close to
reference levels.
In summary, the Commencement Bay study area presents a mixed picture
relative to contamination and biological effects. The bay is not an ecological
disaster area with overall high contamination and pervasive biological
effects. Commencement Bay is a complex estuarine environment in which
the levels of contamination and effects vary considerably. While there
are definite indications of stress to local biological communities (e.g.,
altered benthic assemblages, accumulation of contaminants in fish and shellfish,
and liver lesions in flatfish), most of the area is characterized by high
abundances of benthic organisms and demersal fishes, and the fish do not
appear to be severely stressed by liver lesions or accumulations of toxic
substances.
9.3
-------
10.0 STUDY DESIGN EVALUATION AND RECOMMENDATIONS
FOR FUTURE STUDIES
The Commencment Bay Nearshore/Tideflats Remedial Investigation involved
the collection of extensive data and the implementation of a complex decision-
making process. Because of the unique nature of the study area and the
complexity of potential sources, contaminants, and biological effects,
many of the investigative techniques and decision criteria were developed
specifically for this project. This section provides a retrospective evaluation
of the innovative study approach and presents recommendations for future
studies of sediment contamination in the marine environment.
10.1 SEDIMENT CHEMISTRY
1. The addition of multiple (>50) isotopically labeled recovery
standards to every sample Increased confidence in the validity
of detection limits for undetected target compounds. By
forcing a search for each recovery standard, this recovery
technique also increased the efficiency and reporting of
target compounds that otherwise may have been overlooked
in the complex extracts.
2. Use of a defined list of tentatively identified compounds
to search for in each sample analyzed greatly improved the
value of these data in spatial characterizations of contami-
nation.
3. Low detection limits for organic compounds in the range
of 5 to 50 ppb (dry weight sediment or wet weight tissue)
were useful in defining conditions 1n the reference area,
extent of problem areas, and Interrelationships among chemical
and biological Indicators, and 1n estimating human health
risks. Because major sample Interferences were removed
to attain these limits, Improved precision was possible
1n the quantification of compounds present at high concen-
tration.
4. Historical problems with potential m1sident1fication of
pesticides 1n sediments was successfully avoided by using
mass spectroscopy Instead of electron capture detection.
This advantage outweighed the Increase 1n detection limits
by mass spectroscopy, but electron capture analyses are
still recommended for tissue samples (with mass spectral
confirmation of any high values) to obtain low enough detection
limits for use in health risk assessments.
5. Sampling of suspended solids 1n the water column for toxic
chemicals at two depths and at two times during the study
made possible only a limited qualitative estimate of the
ambient levels or apparent transport of chemicals. Even
10.1
-------
with filtering 100 L of water, detection limits for most
organic compounds other than PAH were too high to be useful.
Water column studies are recommended only for metals, PAH
(by GC/MS), or selected chlorinated compounds amenable to
sensitive GC/ECD analysis. The organic analyses should
be conducted with a minimum of 0.5 g of material.
6. PCB concentrations reported as total PCBs enabled an adequate
characterization of the PCB distribution. This reporting
format is recommended because PCB mixtures in the environment
are rarely representative of original Aroclor components.
7. A two-phase coring program is recommended to determine the
extent of contamination in historical sediments and to overcome
penetration problems caused by textural characteristics
of the sediments. The first phase (lower cost) should use
a coring device (box, Kasten, wide-diameter gravity core)
that can recover intact surface and near-surface sediments;
the second phase (higher cost) should incorporate drilling
techniques to recover deeper sediments if analysis of the
bottom of the phase I core shows elevated contamination.
8. A sampling interval of up to 1 ft in sediment cores was
adequate when the primary goal was focused on potential
required dredging depths for contaminated sediments. However,
the bottom 2 cm of each core should be analyzed in future
studies of this type to reduce uncertainty as to whether
a significant decline in concentration toward the bottom
of the core was masked by compositing over large depth
intervals.
9. Sampling intervals of 1-5 cm thickness should be used in
sediment cores to estimate the chronology of deposition.
This chronology can be critical in determining whether
contamination is historical or ongoing.
10. Substantial quality assurance review and laboratory oversight
were required 1n a study of this complexity. This review
and oversight were based on an Integration of analytical
chemistry techniques with environmental trend analysis.
Such an integration should be required 1n future studies
and should always Include a laboratory site visit before
samples are processed.
.2 BIOLOGICAL EFFECTS
1. The collection of four replicate 0.06-m2 van Veen grab samples
enabled an adequate assessment of benthlc community structure
1n Commencement Bay. Use of a 0.06-m? grab 1s recommended
for future studies because of substantial cost savings (per
sample) over a standard 0.1-m2 grab.
2. Statistical analyses of the abundances of major groups of
benthlc macrolnvertebrates (I.e., total abundance, Poly-
10.2
-------
chaeta, Mollusca, and Crustacea) enabled areas of toxic
effects to be identified. Evaluation of community structure
based on species-level identification was useful in assessing
differences among areas and in identifying probable causes
(e.g., toxicity vs. organic enrichment) of modified benthic
assemblages.
3. Selection of an adequate reference area is critical to evaluation
of effects on benthic macroinvertebrates because of the
overriding influence of sediment particle size on these
assemblages. If detailed information on the sediment charac-
teristics of the study area and candidate reference sites
is not available, a reconnaissance survey should be conducted
to ensure that adequate reference sites are available for
the range of sediment characteristics in the study area.
4. The current study design enabled detection of statistically
significant differences in fish hepatic lesion prevalences
at the waterway level. Therefore, the use of demersal fish
histopathology as an effects variable can provide a relatively
localized assessment of biological effects.
5. Fish histopathology is an important independent indicator
of biological effects because it does not correlate with
effects on benthic macroinvertebrates or sediment toxicity.
6. Analyses of contaminants 1n English sole muscle tissue enabled
assessment of spatial differences in bioaccumulation on
a waterway basis, and in some cases within a waterway.
The site-specific co-occurrence of several compounds in
sediments and fish muscle tissue indicates that these studies
provide a reliable assessment of bioavailability of sediment
contaminants.
7. Use of five fish tissue samples per area results 1n a relatively
poor statistical power 1n detecting spatial differences
in tissue contaminant levels. However, for Important compounds
such as PCBs, the current study design enabled detection
of statistically significant elevations in tissue concentrations
on a waterway basis that were <5 times the reference concen-
tration.
8. Larger English sole (e.g., >300 mm total length) should
be used for bioaccumulation studies to ensure that sufficient
muscle tissue is available for full-scan priority pollutant
analyses.
9. Full-scan priority pollutant analyses of fish livers are
not recommended because of small sample sizes and the consider-
able sample processing required to reduce Interferences
from high lipid content. Analyses of fish livers may be
useful, however, for specific substances such as PCBs or
selected metals (e.g., mercury).
10.3
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10. Volatile organic compounds were bioaccumulated by English
sole in several areas of Commencement Bay. These compounds
(especially tetrachloroethene) should be analyzed for in
fish tissues if there is evidence of high sediment or water
contamination.
11. The oyster larvae bioassay is not recommended for future
studies of sediment contamination because of response similarity
with the amphipod bioassay, confounding problems with high
mortalities, and effects of low dissolved oxygen. To a
lesser degree, the amphipod bioassay may also be subject
to interpretive difficulties because of oxygen depletion
during exposure to highly organically enriched sediments.
12. Amphipod bioassay mortalities may result from particle size
effects where the sediments are >80 percent fine-grained
materials (i.e., silt plus clay). In those cases, sediment
chemistry data should be carefully reviewed, and the influence
of particle size should be evaluated before concluding that
observed mortalities are caused by toxic contamination.
13. Conducting sediment bioassays and benthic infaunal analyses
at each sediment chemistry station would have enabled a
much better determination of quantitative relationships
[toxicity and benthic apparent effect thresholds (AET)].
14. Four kinds of hepatic lesions (neoplasms, preneoplasms,
megalocytic hepatosis, and nuclear pleomorphism) should
be used in assessing histopathology in English sole.
15. For liver histopathology studies, 60 fish per area is the
minimum number required to obtain reasonable statistical
discrimination (i.e., to detect differences in lesion prevalence
of 10-15 percent) among areas.
16. English sole used for liver histopathology studies should
be >225 mm total length and >3 years of age. All samples
should also be age-corrected prior to statistical evaluation
of spatial or temporal differences in lesion prevalence.
.3 DECISION-MAKING APPROACH
1. The defined decision-making approach, Incorporating five
Independent measures of contamination, toxicity, and biological
effects (i.e., sediment chemistry, sediment bioassays, benthic
macrolnvertebrates, fish bloaccumulation, and fish liver
histopathology), enabled an objective and defensible Identifi-
cation and prioritization of problem areas associated with
toxic chemical contamination. For this purpose, the latter
two measures were used only as average values at the waterway
level. The first three measures were also used as site-specific
Indicators to define the spatial extent of problems areas.
The use of this assessment approach ("pentad approach")
is recommended 1n other studies of sediment contamination.
10.4
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2. Using toxicity and benthic AET, the extent of problem areas
could be defined and potential problem chemicals at each
site could be identified. Although AET are first approximations
and not proof of cause-effect relationships, the AET provide
empirical evidence that helps define and narrow the "gray
zone" between a clear no-effects level and an apparent effect
level for different chemicals. Identifying chemicals above
AET values allowed source identification efforts to focus
on those problem chemicals.
10.4 SOURCE IDENTIFICATION
1. Normalization of chemical concentrations to organic carbon
or percent fine-grained material was sometimes useful in
giving additional source information not conveyed by drv-
weight concentrations 1n sediments. At the most severely
contaminated sites, however, gradients in dry-weight concentra-
tions were sufficient to indicate potential sources. Normaliza-
tion of chemical concentrations enabled a better definition
of groups of chemicals with similar environmental distribu-
tions and potentially similar sources. Because organic
carbon and grain size probably affect the bioavailability
of chemicals, the continued evaluation of normalized data
in developing quantitative relationships is also reconmended.
2. Contaminant loading data were limited for most potential
sources, and for many others, no loading data existed.
This data gap impaired source evaluation and allowed prioriti-
zation of potential sources on a relative basis only. Collection
of additional source data 1s recommended in all problem
areas. These data should cover at least critical problem
chemicals, with detection limits that reflect representative
flow conditions and suspended solid loadings from each source
(i.e., consider the detection limits of the resulting loading
for each chemical). Additional measurements of flow rates
are needed to establish reliable estimates of the relative
magnitude of sources.
Estimates of historical contaminant loadings are even more
uncertain than those for ongoing sources. Contaminant loadings
in a problem area may have changed over time because different
industries occupied the site or because changes in industrial
activities altered the contaminant loadings in the discharges.
Therefore, additional review of historical Industrial and
land use practices are recommended, with a focus on the
problem chemicals and products that contain these chemicals.
3. In several of the problem areas it was difficult, or Impossible,
to determine whether the contamination observed in the sediments
was from historical or ongoing sources. Data gaps that
prevented this determination Included inadequate or missing
source loading data for the problem chemicals, and inadequate
sedimentation rate estimates for the individual waterways.
10.5
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Additionally, disturbance from dredging activities within
the problem areas complicated the assessment of relative
depositional periods of the problem chemicals. This was
the case for PCBs in Hylebos Waterway Segment 2. Source
investigations have revealed little about whether PCBs are
from historical or ongoing sources.
4. Sediment accumulation rates in major problem areas in waterways
such as City and Hylebos obviously differ substantially
from one another, but are needed to address remedial alterna-
tives. Representative rates are unknown. While conditions
in these waterways present problems in applying dating tech-
niques, dating of selected cores (e.g., by the Pb-210 technique)
is recommended to determine if gross estimates of sediment
accumulation rates (mg'kg'^yr'l) may be possible in these
areas.
10.6
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