uget Sound Estuary Program
BUDD INLET ACTION PLAN:
Initial Data Summaries
and Problem Identification
TC-3338-27
FINAL REPORT
April 1988
Prepared for
U.S. Environmental Protection Agency
Region X - Office of Puget Sound
Seattle, Washington
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Final Report
TC-3338-27
BUDD INLET ACTION PLAN:
INITIAL DATA SUMMARIES AND
PROBLEM IDENTIFICATION
by
Tetra Tech, Inc.
for
U.S. Environmental Protection Agency
Region X - Office of Puget Sound
Seattle, Washington
April 1988
Tetra Tech, Inc.
11820 Northup Way, Suite 100
Bellevue, Washington 98005
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CONTENTS
Page
LIST OF FIGURES iv
LIST OF TABLES vi
EXECUTIVE SUMMARY viii
BUDD INLET ACTION PLAN viii
PHYSICAL SETTING viii
DECISION-MAKING FRAMEWORK ix
CONTAMINANT SOURCES ix
EUTROPHICATION x
MICROBIAL CONTAMINATION xi
SEDIMENT CONTAMINATION OF SEDIMENTS AND BIOTA xii
IDENTIFICATION OF PROBLEM AREAS xiii
IDENTIFICATION OF DATA GAPS xiv
INTRODUCTION 1
DECISION-MAKING FRAMEWORK FOR EVALUATION OF ENVIRONMENTAL DEGRADATION 4
OVERVIEW OF DECISION-MAKING PROCESS 4
IDENTIFICATION AND EVALUATION OF POLLUTANT VARIABLES 7
INDICES OF CONTAMINATION 10
PROBLEM AREA IDENTIFICATION 17
PHYSICAL SETTING 20
PROJECT LOCATION 20
PHYSICAL OCEANOGRAPHY 20
GEOLOGY 22
DRAINAGE PATTERNS 23
CLIMATE 25
LAND USE 25
BENEFICIAL USE 26
DATA SUMMARIES 28
CONTAMINANT SOURCES 28
EUTROPHICATION 54
MICROBIAL CONTAMINATION 75
CHEMICAL CONTAMINATION OF SEDIMENTS AND BIOTA 82
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IDENTIFICATION OF PROBLEM AREAS 121
EUTROPHICATION 121
MICROBIAL CONTAMINATION 122
TOXIC CONTAMINATION 124
IDENTIFICATION OF DATA GAPS 127
EUTROPHICATION 127
MICROBIAL CONTAMINATION 128
TOXIC CONTAMINATION 129
OTHER DATA GAPS 133
REFERENCES 134
APPENDIX A - DATA EVALUATION SUMMARY TABLES A-l
APPENDIX B - MONTHLY AVERAGES OF WATER QUALITY DATA AT ECOLOGY
AMBIENT MONITORING STATIONS BUD002 AND BUD005 B-l
APPENDIX C - HISTORY OF SEDIMENT DREDGING IN BUDD INLET C-l
APPENDIX D - CONTAMINANT CONCENTRATIONS IN BUDD INLET SEDIMENTS D-l
APPENDIX E - BUDD INLET BIBLIOGRAPHY E-l
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FIGURES
Number Page
1 Budd Inlet study area 2
2 Comprehensive decision-making framework for evaluation of
environmental degradation 5
3 Preponderance-of-evidence approach to evaluate eutrophication,
microbial contamination, and toxic chemical contamination in
Budd Inlet 6
4 Budd Inlet and Deschutes River drainage boundaries 24
5 Locations of potential point and nonpoint discharges of
contaminants to Budd Inlet 29
6 Locations of storm drain outfalls in Budd Inlet 32
7 Locations of water quality and fecal coliform bacteria
sampling stations in Budd Inlet 56
8 Theoretical example of vertical profile of dissolved oxygen 57
9 Annual variation in nitrogen and orthophosphate in surface
waters at the WDNR Marine Station, 1981-1982 60
10 Temporal variation in nitrogen [sum of nitrate (N03) and
ammonium (NH^)] at Ecology ambient water quality monitoring
stations BUD002 and BUD005, 1982-1986 61
11 Temporal variation in phosphate at Ecology ambient water
quality monitoring stations BUD002 and BUD005, 1982-1986 64
12 Distribution of dissolved oxygen in the bottom waters of
upper Budd Inlet, 17-18 August 1977 67
13 Monthly variation in dissolved oxygen (DO) measured at the
five LOTT WWTP monitoring stations in 1986 68
14 Temporal variation in dissolved oxygen (DO) at Ecology ambient
water quality monitoring stations BUD002 and BUD005, 1982-1986 70
15 Daily variation in dissolved oxygen (DO) in the surface,
middle, and bottom waters near the East Bay Marina,
summer 1986 72
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16 EAR values for concentrations of fecal coliform bacteria
in water samples from Budd Inlet 81
17 Percent total volatile solids (TVS) measured in sediments at
stations in the East and West Bays of Budd Inlet 83
18 Percent total volatile solids (TVS) and percent total organic
carbon (TOC) measured in sediments at stations in the East and
West Bays of Budd Inlet 84
19 Locations of sediment chemistry, water chemistry, shellfish
bioaccumulation, and sediment toxicity sampling stations in
the East and West Bays of Budd Inlet, 1982-1987 86
20 Locations of sediment chemistry, water chemistry, and shellfish
bioaccumulation sampling stations at the north end of the Port
of Olympia peninsula 87
21 EAR values for concentrations of LPAH in sediments from the
East and West Bays of Budd Inlet 99
22 EAR values for concentrations of HPAH in sediments from the
East and West Bays of Budd Inlet 100
23 EAR values for concentrations of copper, lead, and zinc in
sediments from the East and West Bays of Budd Inlet 101
24 EAR values for concentrations of copper, lead, and zinc in
sediments from the East and West Bays of Budd Inlet 102
25 EAR values for concentrations of cadmium in sediments from
the East and West Bays of Budd Inlet 103
26 EAR values for concentrations of arsenic in sediments from
the East and West Bays of Budd Inlet 104
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TABLES
Number Page
1 Primary kinds of data used in problem area identification
and priority ranking 9
2 Preliminary list of contaminants and conventional variables
of concern in Budd Inlet 11
3 Criteria for prioritizing problem areas in Budd Inlet 19
4 List of NPDES-permitted waste discharges to Budd Inlet 30
5 Concentrations (ug/L) of volatile and extractable organic
compounds in product and groundwater seep samples collected in
June 1987 from Cascade Pole Company 50
6 Relative contribution of sources of nitrogen to Budd Inlet 63
7 Fecal coliform bacteria data and mean EAR values for Budd
Inlet, 1982-1987 79
8 Data limitations of selected studies used in detailed analysis
of sediment chemistry 91
9 Summary of metal concentrations in sediments from Puget Sound
reference areas 93
10 Summary of organic compound concentrations in sediments from
Puget Sound reference areas 94
11 Concentrations and EAR values for selected chemical indicators
in Budd Inlet 105
12 Comparisons of contaminant concentrations in Budd Inlet
sediments with Puget Sound AET values 107
13 Summary of bioaccumulation data for Budd Inlet 111
14 Summary of EAR values for amphipod and oyster larvae
sediment bioassays 116
15 List of primary and secondary problem areas in Budd Inlet 123
VI
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A-l Data evaluation summary for water quality studies A-2
A-2 Data evaluation summary for contaminant source studies A-3
A-3 Data evaluation summary for sediment contamination and
bioaccumulation studies A-4
A-4 Data evaluation summary for sediment toxicity studies A-5
A-5 Summary of accepted water quality studies A-6
A-6 Summary of accepted contaminant source studies A-7
A-7 Summary of accepted sediment contamination and
bioaccumulation studies A-8
A-8 Summary of accepted sediment toxicity studies A-9
B-l Monthly averages of water quality data collected from 1982
to 1986 at Ecology ambient water quality monitoring Stations
BUD002 and BUD005 B-l
C-l List of dredging permits issued for Budd Inlet since 1980 C-2
D-l Contaminant concentrations in Budd Inlet sediments D-l
Vll
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EXECUTIVE SUMMARY
BUDD INLET ACTION PLAN
The Puget Sound Estuary Program (PSEP) is a forum for interagency
cooperation to identify and recommend solutions to water quality problems in
Puget Sound. Under this program, the U.S. Environmental Protection Agency
(EPA) has identified Budd Inlet as a priority area for evaluation of
environmental degradation. The goals of the Budd Inlet Action Plan are to
protect the marine and estuarine ecosystem of Budd Inlet against further
degradation from anthropogenic inputs of contaminants, to identify degraded
areas that are amenable to restorative action, and to protect recreational
uses from contamination.
This report provides a synthesis of information describing the
geographic extent and severity of environmental degradation in Budd Inlet.
Summaries of existing data are provided for the following indicators of
environmental degradation: contaminant sources, eutrophication, microbial
contamination, and chemical contamination of sediment and biota. Data that
were collected from 1982 to 1987 are presented in this report. The year
1982 is significant because the Cities of Lacey, Olympia, and Tumwater, and
Thurston County (LOTT) wastewater treatment plant (WWTP) began secondary
treatment in August 1982. Recent data are also used to represent present
conditions in Budd Inlet, and to ensure that data were collected and
analyzed using current methods. Occasionally, older data were used when
more recent data were unavailable in the same geographic area.
PHYSICAL SETTING
Budd Inlet is a shallow estuary at the extreme southern end of Puget
Sound. It includes the area south of a line joining Cooper Point and Dover
Point (see Figure 1 in "Introduction"). The Deschutes River is the major
freshwater source to Budd Inlet. Most urban and industrial activity is
viii
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located in the Cities of Olympia and Tumwater at the southern end of the
inlet. Although Capitol Lake is a point source to Budd Inlet, it is not
included in the study area.
DECISION-MAKING FRAMEWORK
A decision-making framework was developed to evaluate environmental
degradation in Budd Inlet. The decision-making framework includes 1) a
review of available environmental data, 2) analyses of spatial and temporal
trends of eutrophication, microbial contamination, and toxic contamination
in Budd Inlet, 3) a limited ranking of problem areas for interim corrective
actions, and 4) identification of data gaps. The decision-making framework
used in this report is based on the framework developed for the Elliott Bay
(Tetra Tech 1985b) and Everett Harbor (Tetra Tech 1985c) Action Plans.
Data were compiled and evaluated according to the following pollutant
categories: contaminant sources (including groundwater and surface water),
eutrophication, microbial contamination, and chemical contamination of
sediment and biota, including sediment contamination, bioaccumulation in
shellfish, sediment and water toxicity bioassays, benthic infaunal com-
munities, and fish pathology. These key variables were then used to develop
indices of contamination and biological effects that are based on comparisons
with either a reference site in Budd Inlet, reference conditions for Puget
Sound [i.e., elevation above reference (EAR) values], or regulatory standards
[e.g., apparent effects threshold (AET) values] and criteria. Resultant
information was used to identify problem areas.
CONTAMINANT SOURCES
The following six major categories of point and nonpoint sources of
contaminants to Budd Inlet were identified and discussed: WWTP, combined
sewer overflows (CSO), surface runoff, industrial sources, groundwater, and
accidental spills. The LOTT, Tamoshan, Beverly Beach, and Seashore Villa
WWTP discharge to Budd Inlet. The City of Olympia currently has one CSO
that discharges to West Bay and one CSO that discharges to East Bay via
Moxlie Creek. These CSOs are reported to flow infrequently. The LOTT WWTP
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currently has one manually operated emergency overflow that enters Budd
Inlet. Over 50 City of Olympia storm drain outfalls discharge to Budd
Inlet. Except for the West Bay drain on Port of Olympia property, CSOs and
storm drains have not been investigated for annual flow estimates or chemical
composition. In addition to the four WWTP, two National Pollutant Discharge
Elimination System (NPDES) permits are issued to Chevron U.S.A. and Delson
Lumber Company/Olympia Forest Products. Based on analyses of sediment and
groundwater data, an NPDES permit may be required for the Cascade Pole
Company site. Analytical results from sediment and effluent samples
collected at the Cascade Pole Company former NPDES-permitted outfall and the
West Bay drain, and groundwater and product seep samples from the Cascade
Pole site indicate that these areas are highly contaminated with polynuclear
aromatic hydrocarbons (PAH).
Other ongoing and historical contaminant sources may include unpermitted
waste discharges, a former metal plating facility, the U.S. Maritime
Mothball Fleet, plywood fabricating facilities, five marinas, historical
landfills, bulk petroleum storage facilities, petroleum spills, and surface
runoff. Over 80 percent of the surface runoff flows into Budd Inlet via
natural drainage channels. The major pollutant sources to Budd Inlet are
the Cascade Pole Company and the LOTT WWTP.
EUTROPHICATION
Water quality studies were reviewed to identify the relationship
between nutrient concentrations and dissolved oxygen in Budd Inlet. Data
were compiled from the records of four WWTP, the Port of Olympia (i.e., East
Bay Marina), the Ecology ambient water quality monitoring program, URS
(1986), and the Washington Department of Natural Resources Marine Station.
Spatial and temporal trends of concentrations of dissolved oxygen and
nutrients were analyzed, and dissolved oxygen data were compared with
Washington State standards. A seasonal depletion in nitrogen was evident at
stations away from the LOTT WWTP outfall. A seasonal decline in dissolved
oxygen was observed at all sampling stations established to monitor water
quality. Oxygen depletion occurred to levels below 3.0 mg/L at Ecology
Station BUD002 in West Bay, at the Capitol Lake outfall, and in the East Bay
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Marina. The Washington State Class B water quality standard (5.0 mg/L) was
violated at each of the previously mentioned stations, in the Fiddlehead
Marina, north of the LOTT 30-in diameter outfall, and in the navigation
channel northeast of the Cascade Pole Company. The distribution of dissolved
oxygen at the water-sediment interface was not investigated, although oxygen
levels may be lowest at this interface due to sediment oxygen demand
(Rhoads, D., 18 November 1987, personal communication).
MICROBIAL CONTAMINATION
Microbial concentrations (i.e., fecal coliform bacteria) in Budd Inlet
have been determined primarily by a comprehensive study of circulation and
water quality in Budd Inlet (URS 1986), in the ambient water quality
monitoring program conducted by Ecology (U.S. EPA, 7 January 1988, personal
communication), by the City of Olympia (Alan, R., 24 September 1987,
personal communication), and by U.S. EPA/Washington Department of Social and
Health Services (Armstrong, J., 17 November 1987, personal communication).
Results of these studies indicate that water quality standards for fecal
coliform bacteria, as measured by the geometric mean concentrations, were
violated in several areas. Moxlie Creek was the only site to exceed
Washington State Class B water quality standards. High geometric mean
concentrations were also calculated for Ellis Cove, Butler Cove, Boston
Harbor, Priest Point, southern Tykle Cove, and areas near the Tamoshan WWTP,
Beverly Beach WWTP, Seashore Villa WWTP, and Athens Beach. Seasonal
variability of fecal coliform bacteria concentrations were not observed at
offshore stations, but were observed at nearshore stations. Data collected
by URS (1986) indicated that the major sources of bacteria loading were
Moxlie Creek, LOTT WWTP, and Capitol Lake (as determined at the tidal gate).
Nonpoint sources of microbial contamination in Budd Inlet include
contributions from surface runoff from hobby farms, live-aboards in five
Olympia marinas, and general boating activity. These sources have not been
qualitatively or quantitatively investigated.
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CHEMICAL CONTAMINATION OF SEDIMENTS AND BIOTA
Sediment Contamination
Limited data on sediment contamination are available for Budd Inlet.
EAR values were calculated for the available data, and these data were also
compared with Puget Sound AET values. Elevated concentrations of organic
compounds have been detected in sediments near the Cascade Pole Company
(Johnson, A., 22 July 1985, personal communication; Norton, 5 February 1986,
personal communication). Concentrations of PAH in sediments from this area
were higher than concentrations of PAH observed in Commencement Bay (Tetra
Tech 1985a), Elliott Bay (Tetra Tech 19855), and Everett Harbor (Tetra Tech
1985c). Elevated concentrations of organic compounds were also detected
near the West Bay drain, which is adjacent to the Cascade Pole Company site
(Norton, D., 5 February 1986, personal communication). Concentrations of
copper, lead, zinc, and cadmium appeared to be elevated near the Fiddlehead
Marina (Alan, R., 24 September 1987a, personal communication).
Bioaccumulation
Recent bioaccumulation data for marine organisms in Budd Inlet are
limited to the concentrations of PAH in clams collected near Cascade Pole
Company and Priest Point (Norton, D., 5 February 1986, personal commun-
ication). Concentrations of PAH in those clams were similar to high
concentrations reported for clams from Eagle Harbor (Yake et al. 1984).
Concentrations of PAH in clams collected near the West Bay storm drain were
similar to the lower range of values found in other Puget Sound urban bays.
Mai ins et al. (1980) found that concentrations of certain non-toxic metals
in English sole were considerably higher in Budd Inlet than in other urban
areas, while concentrations of organic compounds in fish from Budd Inlet
were generally less than concentrations observed in other urban bays.
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Toxicity Bioassavs
Bioassay tests using the amphipod Rhepoxvnius abronius were conducted on
sediments collected from a station located north of the Cascade Pole Company
near the navigation channel (Schiewe, M., 19 November 1987, personal
communication), and on sediments from near the Olympia Yacht Club [U.S. Army
COE, no date (c)]. Results of these bioassays indicate that neither site is
a potential problem area. Oyster larvae (Crassostrea gigas) bioassays were
also conducted on sediments collected north of the Cascade Pole Company. Low
mortality rates were reported.
Benthic Infaunal Communities
No benthic community data are available from 1982 to 1987 in Budd
Inlet. An earlier study (Evergreen State College 1974) identified an
apparently diverse community in the upper inlet. However, data collection
and laboratory analysis methods used in this study were inadequate to allow
for characterization of benthic infaunal communities and identification of
problem areas.
Fish Pathology
From 1982 to 1987, no fish pathology data were collected in Budd Inlet.
Earlier data collected by Mai ins et al. (1980) indicated that certain
pathological abnormalities were present in English sole and rock sole
collected within Budd Inlet. The incidence of these abnormalities varied
between 0 and 30 percent.
IDENTIFICATION OF PROBLEM AREAS
The selected data for indicators of eutrophication, microbial contamina-
tion, and chemical contamination in sediments and biota were integrated to
identify and prioritize problem areas in Budd Inlet. The evaluation
included comparisons with regulatory standards, sediment quality criteria
(i.e., AET values), and EAR values.
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The highest priority problem areas for eutrophication were Ecology
Station BUD002 in West Bay, the Capitol Lake outfall, and the East Bay
Marina. Dissolved oxygen levels at these sites were less than 3.0 mg/L
during late summer. Secondary priority areas for eutrophication were
located at the Fiddlehead Marina, north of the LOTT 30-in diameter outfall,
and in the navigation channel northeast of Cascade Pole Company. The
highest priority problem areas for microbial contamination occurred at
Moxlie Creek, Boston Harbor, Ellis Creek, and south of Tykle Cove. Concen-
trations of fecal coliform bacteria in these areas exceeded 10 times the
Washington State water quality standard. Secondary priority problem areas
for microbial contamination were identified at Tamoshan WWTP, Beverly Beach
WWTP, Athens Beach WWTP, Butler Cove, and north of Priest Point. The
highest priority problem areas for sediment chemistry were located near the
Cascade Pole Company and the West Bay drain. Concentrations of organic
compounds in sediments exceeded 100 times the reference values at these
locations. Secondary priority problem areas were located in West Bay
offshore from the West Bay drain, and in Fiddlehead Marina. No problem
areas were identified using sediment toxicity tests. Problem areas based on
benthic infaunal communities and fish pathology indicators could not be
identified because data are unavailable.
IDENTIFICATION OF DATA GAPS
Limited data are available for each category of data reviewed for Budd
Inlet. The available data confirm that a seasonal problem of low concentra-
tions of dissolved oxygen occurs in East and West Bays. However, the
geographic extent and short-term temporal variability of the problem are
unknown. Dissolved oxygen should be monitored in the upper inlet during the
seasonal decline in oxygen (i.e., July to September) to enable the boundaries
of low dissolved oxygen concentrations to be identified. Microbial
contamination problem areas were identified using the available data. A
monitoring program of fecal coliform bacteria concentrations at known
sources would allow an assessment of the magnitude of microbial contamination
under varying water flow conditions. Sediment contamination has been
identified near the Cascade Pole Company. Additional studies are needed to
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determine the spatial extent of contamination. Sediments near known point
sources (e.g., Moxlie Creek) should also be investigated. Except for
bioaccumulation of PAH in clams collected near the Cascade Pole Company,
biological effects of sediment contamination remain uninvestigated.
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INTRODUCTION
The U.S. Environmental Protection Agency (EPA) and the Washington
Department of Ecology (Ecology), in cooperation with other federal, state,
and local agencies, are investigating the extent and severity of environ-
mental degradation in Budd Inlet (Figure 1). The identification of degraded
areas may lead to remedial action to correct problems associated with
eutrophication, microbial contamination, and toxic contamination. Remedial
actions may include source control to reduce nutrient, microbial, and
toxicant emissions; and cleanup of contaminated sediments. This report
provides a synthesis of information describing the geographic extent and
severity of environmental degradation in Budd Inlet. Those data that were
collected from 1982 to 1987 are presented in this report. The year 1982 is
significant because the Lacey, Olympia, Tumwater and Thurston County (LOTT)
wastewater treatment plant (WWTP) began secondary treatment in August 1982.
Occasionally, older data were used when more recent data were unavailable in
the same geographic area. The evaluation focuses on the following questions
concerning the study area:
1. Is Budd Inlet, or parts of Budd Inlet, subject to environ-
mental degradation due to eutrophication, microbial contam-
ination, or toxic contamination?
2. Does eutrophication or toxic contamination result in adverse
biological effects?
3. Is there a potential threat to public health?
4. Can the sources of contamination be identified?
Answering these questions involved the synthesis of complex information
including data on contaminant sources, fates, and effects, and resulted in a
preliminary identification of presently known problem areas (e.g., areas
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ro
PUGET
SOUND
BUDD
INLET
OLYMPIA
CITY
BOUNDARY
OLYMPIA
nautical mil**
kilometers
Figure 1. Budd Inlet study area.
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with high concentrations of nutrients and fecal coliform bacteria, low
levels of dissolved oxygen, contaminated sediments, and contaminated
shellfish). Gaps in the existing data are summarized and recommendations
are made for additional data collection to enable a more comprehensive
assessment of the geographic extent and severity of problem areas.
Environmental degradation associated with eutrophication and microbial
contamination was evaluated by comparing the data with Washington State
water quality standards. Although gaps in the available information were
present on both temporal and spatial scales, sufficient data were available
to identify areas subject to water quality degradation. The decision-making
approach for toxic contamination and biological effects that was used in the
development of similar action plans for Elliott Bay (Tetra Tech 1985b) and
Everett Harbor (Tetra Tech 1985c) was adapted to evaluate toxic and microbial
contamination problems.
The report is organized into five major sections. The first section
describes the decision-making approaches for evaluating environmental
problems associated with eutrophication and toxic contamination. The
discussion includes the rationale for choosing the water quality, chemical,
ecological, and toxicological indicators used for evaluating environmental
degradation. The second section provides descriptions of the physical
setting, including project location, physical oceanography, geology,
drainage patterns, climate, land use, and beneficial use. The third section
provides summaries of existing data for the following indicators of
environmental degradation: 1) contaminant sources, 2) eutrophication, 3)
microbial contamination, and 4) chemical contamination of sediment and
biota. The fourth section identifies problem areas based on existing
information for the environmental indicators. Although other indicators
could be used to identify problem areas (e.g., fish distribution, fish
kills), the selected variables are statistically sensitive to a wide range
of ecosystem properties. The final section provides a description of
existing data gaps and additional information required for a more thorough
delineation and better understanding of the problem areas.
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DECISION-MAKING FRAMEWORK FOR EVALUATION OF
ENVIRONMENTAL DEGRADATION
Eutrophication, microbial pathogens, and toxic chemical contamination
are the three areas of concern for evaluating environmental degradation of
Budd Inlet. Information on the geographic extent and severity of these
pollution problems was compiled and used in a decision-making framework to
prioritize areas within Budd Inlet for cleanup or source control. The
decision-making framework is a method designed to consolidate and integrate
detailed environmental information in a form that can be readily used and
evaluated by regulatory decision-makers and easily revised as new information
becomes available (Figure 2). The decision-making approach used for Budd
Inlet was adapted from that used for the Elliott Bay and Everett Harbor
Action Plans (Tetra Tech 1985b,c) to 1) include an evaluation of eutrophica-
tion and microbial contamination, and 2) accommodate the use of qualitative
or semiquantitative information because of the lack of synoptic data.
Details of the decision-making framework and its application in Budd Inlet
are provided below.
OVERVIEW OF DECISION-MAKING FRAMEWORK
The decision-making approach developed for the Budd Inlet Action Plan
incorporates a "preponderance-of-evidence" approach to identify problem
areas associated with pollution problems (Figure 3). First, information
concerning sources of pollution associated with eutrophication, microbial
contamination, and toxic chemical contamination were reviewed to identify
potential problem areas. The available physical, chemical, and biological
data for each pollutant category were then reviewed. Key variables that
could be used meaningfully in a qualitative or quantitative characterization
of the spatial and temporal extent of pollutant impacts were identified.
Quantitative relationships and statistically significant associations among
these key variables were also identified where possible. The various key
variables were then used to develop indices of contamination and biological
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REVIEW AVAILABLE
INFORMATION
IDENTIFY
REFERENCE AREAS
IDENTIFY SUBSTANCES
OFCONCERN
COMPARE BUDD INLET
SITES WITH
REFERENCE AREA
EVALUATE
DATA GAPS
RANK BUDD INLET SITES BASED ON COMPARISONS
WITH SEDIMENT QUALITY CRITERIA, WATER
QUALITY STANDARDS, AND/OR EAR VALUES
RANK SUBSTANCES BASED ON COMPARISONS
WITH SEDIMENT QUALITY CRITERIA, WATER
QUALfTY STANDARDS, AND/OR EAR VALUES
DEVELOP SAMPLING
PLAN DESIGN
RECOMMEND
PRELIMINARY
ACTION-LEVEL CRITERIA
EVALUATE NEW
INFORMATION
IDENTIFY
PROBLEM AREAS
RE-EVALUATE
ACTION-LEVEL CRITERIA
Figure 2. Comprehensive decision-making framework for
evaluation of environmental degradation.
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POLLUTANT
CATEGORIES
KEY
VARIABLES
EUTROPHICATON
MICROBIAL CONTAMINATION
TOXIC CHEMICAL CONTAMINATION
NUTRIENTS
DISSOLVED OXYGEN
FECAL COLIFORM BACTERIA
• WATER COLUMN
• SHELLFISH
TARGET CHEMICALS
SEDIMENT CONCENTRATIONS
SEDIMENT TOXICITY
BOACCUMULATON
INDICES OF
CONTAMINATION
DISSOLVED OXYGEN
VS.
WATER QUALITY STANDARDS
FECAL COLIFORM BACTERIA
VS.
REFERENCE CONDITION
(WATER QUALITY AND SHELLFISH
STANDARDS)
SEDIMENT QUALITY
• ELEVATION ABOVE REFERENCE
• APPARENT EFFECTS THRESHOLD
SEDIMENT TOXIC me
• OYSTER ABNORMALITY
ELEVATION ABOVE REFERENCE
• AMPHIPOD MORTALITY
ELEVATION ABOVE REFERENCE
CONTAMINANT BIOACCUMULATION
• ELEVATION ABOVE REFERENCE
• HUMAN HEALTH RISK
en
SITE
CATEGORIZATION
SITE
RANKING AND
PRIORITIZATION
HIGHEST PRIORITY
SECONDARY PRIORITY
NO IMMEDIATE ACTION
HIGHEST PRIORITY
• SECONDARY PRIORITY
NO IMMEDIATE ACTION
• HIGHEST PRIORITY
SECONDARY PRIORITY
NO IMMEDIATE ACTON
PROBLEM AREA DEFINITION
• NUMBER OF HIGH
PRIORITY INDICES
IDENTIFICATION OF DATA GAPS
Figure 3. Preponderance-of-evidence approach to evaluate eutrophication, microbial
contamination, and toxic chemical contamination in Budd Inlet.
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effects that are based on comparisons with either a reference site in Budd
Inlet, reference conditions for Puget Sound, or regulatory standards and
criteria. These indices of contamination or biological effects were used to
rank various sites within Budd Inlet, identify key problem areas, and
prioritize sites for further action.
IDENTIFICATION AND EVALUATION OF POLLUTANT VARIABLES
The identification and evaluation of pollutant variables is a multi-step
process that involves:
• An overview of the processes and kinds of physical, chemical,
and biological data that may be used to characterize
eutrophication, microbial contamination, and toxic chemical
contamination
• An evaluation of available site-specific information
• A final selection of variables and site-specific data that
can be used to characterize the spatial and temporal extent
of impacts in Budd Inlet, and to develop indices of contamina-
tion or biological effects.
Key variables used in the decision-making framework to characterize each
category of pollution are briefly summarized below, and described in detail
in the section entitled "Data Summaries."
Eutrophication
Nitrogen is the primary nutrient of concern because it is the limiting
nutrient in Budd Inlet (URS 1986). Nitrogen enters the inlet through the
circulation of Puget Sound water, point sources such as the LOTT WWTP, and
nonpoint sources. Seasonal fluctuations of nitrogen result from dense
nitrogen-consuming phytoplankton blooms during the summer and decreased
flushing rates with the associated reduction in nitrogen renewal. The
development of dense phytoplankton blooms in a poorly flushed area such as
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upper Budd Inlet ultimately leads to dissolved oxygen depletion caused by
decomposition of the phytoplankton. The magnitude of oxygen depletion is a
function of organic enrichment, temperature, and flushing. Oxygen depletion
in the bottom water may stress the resident biota and may cause widespread
mortality if low oxygen levels are prolonged. Although phosphate is not
limiting to phytoplankton in Budd Inlet, it is discharged into Budd Inlet
through the LOTT WWTP.
Key variables used in the characterization of eutrophication in Budd
Inlet were nutrient concentrations (nitrate, nitrite, ammonium, and
phosphate) and dissolved oxygen concentrations. Note that these variables
are influenced by other factors such as temperature, salinity, rainfall,
tidal exchange, and flushing rates. Where possible, these additional
factors were considered qualitatively, but were otherwise not used to rank
and prioritize sites on the basis of eutrophication.
Microbial Contamination
The concentrations of fecal coliform bacteria in the water column and in
shellfish provide an indication of the presence of sewage-derived material
from point and nonpoint sources, and are also indicative of a variety of
other bacterial and viral pathogens that pose a public health risk. Thus,
concentrations of fecal coliform bacteria in water and shellfish were used
to evaluate microbial contamination of water and shellfish in Budd Inlet.
Data on concentrations of other microbial pathogens were not available for
Budd Inlet.
Toxic Chemical Contamination
The primary kinds of data related to toxic contamination that are used
in problem area identification and priority ranking are shown in Table 1.
Although many other variables are evaluated throughout the decision-making
approach, those shown in Table 1 form the basis for the identification of
toxic problem areas. The kinds of data evaluated include chemical concentra-
tions in sediments, and biological effects potentially associated with
chemically contaminated sediments and water.
8
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TABLE 1. PRIMARY KINDS OF DATA USED IN PROBLEM
AREA IDENTIFICATION AND PRIORITY RANKING
General Category
Data Type
Specific Indicator Variables
Habitat condition
Toxicity
Indigenous organisms
Sediment quality
Acute lethal
Sublethal
Bioaccumulation
Benthic community
structure
Fish pathology
Contaminant concentrations
Amphipod mortality
Oyster larvae abnormality
Contaminant concentrations
in tissues of shellfish
Total abundance
Species richness
Dominance
Amphipod abundance
Prevalence of liver
lesions in English sole
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A preliminary list of conventional and chemical contaminants of
concern for Budd Inlet is given in Table 2. Chemical substances on this
list are of concern because they may bioaccumulate or are potentially toxic
to marine organisms and humans. U.S. EPA priority pollutants that may have
been discharged into the study area in the past, or are probably discharged
now, are included on the list. Compounds not on the U.S. EPA list of
priority pollutants also have been considered on the basis of their local
potential significance. Conventional sediment quality variables (i.e.,
grain size, total volatile solids, and total organic carbon) are also
evaluated because they provide a means of comparing areas with different
bulk chemical or physical properties. The list of target chemicals was then
used to identify and select all chemicals or chemical groups of concern from
the available data for Budd Inlet.
Selection of individual biological and toxicological variables was
based on the following considerations:
• Use of the variable in past or ongoing studies in Puget Sound
• Documented sensitivity of the variable to contaminant effects
• Ability to quantify the variable within the resource and time
constraints of the program.
Biological effects variables that were evaluated included a variety of
bioassays used to measure toxicity of receiving waters and sediments;
bioaccumulation of contaminants in shellfish; benthic infaunal community
structure; and pathological disorders in fishes.
INDICES OF CONTAMINATION
The foregoing environmental variables were used to develop a variety of
indices to assess the relative magnitude of contamination in Budd Inlet, to
identify problem chemicals, and to rank and prioritize sites for remedial
action. The various indices used in each category of pollution (i.e.,
10
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TABLE 2. PRELIMINARY LIST OF CONTAMINANTS AND CONVENTIONAL
VARIABLES OF CONCERN IN BUDD INLET
Metals
Silver
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Antimony
Selenium
Zinc
Volatiles
Benzene
Bromoforin
Carbon tetrachloride
Chloroform
Chloroethane
Chlorodibromomethane
Dichloromethane
Dichlorobromomethane
Ethyl benzene
Tetrachloroethane
1,1,1-Trichloroethylene
Toluene
1,1-Dichloroethane
1,1-Di ch1oroethylene
1,2-trans-Dichloroethylene
Xylene
Base/Neutrals (excluding PCBs)
Halogenated Compounds
Hexachloroethane
1,2-Dichlorobenzene
1,3-Dichlorobenzene
1,4-Dichlorobenzene
1,2,4-Trichlorobenzene
2-Chloronaphthalene
Hexachlorobenzene
Hexachlorobutadi ene
Bis(2-chloroethoxy)methane
N-nitrosodiphenylamine
Base/Neutrals (cont.)
Low Molecular Weight Aromatic
Hydrocarbons
Azobenzene
Naphthalene
2-Methylnaphthalene
1-Methylnaphthalene
2,6-Dimethyl naphtha!ene
1,3-Dimethyl naphthalene
2,3-Dimethylnaphtha! ene
2,3,6-Trimethyl naphthalene
2,3,5-Trimethylnaphthalene
Acenaphthene
Acenaphthylene
Fluorene
Biphenyl
1-Methylphenanthrene
2-Methylphenanthrene
3-Methylphenanthrene
High Molecular Weight Aromatic
Hydrocarbons
Fluoranthene
Pyrene
1-Methylpyrene
Benzo(a)anthracene
Dibenzo(a,h)anthracene
Benzofluoranthenes
Benzo(e)pyrene
Benzo(a)pyrene
Indeno(l,2,3-cd)pyrene
Benzo(g,h,i)perylene
Phthalate Esters
Diethyl phthalate
Bis(2-ethylhexyl) phthalate
Butyl benzyl phthalate
Di-n-butyl phthalate
Dimethyl phthalate
Di-n-octyl phthalate
11
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TABLE 2. (Continued)
Acid Extractables
Cresol
Phenol
2-Chlorophenol
2,4-Dichlorophenol
2,4,6-Trichlorophenol
Pentachlorophenol
p-Chloro-m-cresol
4-Nitrophenol
Pesticides and PCBs
Chlordane
Aldrin
Endosulfan
alpha-Hexachlorocyclohexane (HCH)
beta-HCH
delta-HCH
gamma-HCH (lindane)
4,4'-DDD
4,4'-DDE
4,4'-DDT
PCB-1242
PCB-1248
PCB-1254
PCB-1260
Hazardous Substance List Compounds
Benzoic acid
2-Methylphenol
4-Methylphenol
2,4,5-Trichlorophenol
Aniline
Benzyl alcohol
4-Chloroaniline
Dibenzofuran
2-Nitroaniline
3-Nitroaniline
4-Nitroaniline
Miscellaneous Substances
Manganese
Iron
Coprostanol
alpha-Tocopherol acetate
Carbazoles
Retene
Dibenzothiophene
Ch1oromethy1 benzene
Methylated benzenes
1-Propenalbenzene
2-Ethyl naphthalene
3,4,5,6-Tetramethyl phenanthrene
4H-Cyclopenta[DEF]phenanthrene
HH-Benzo(a)fluorene
Benzo(b)thiophene
1-Ethylidene-lH-indene
Dibenzofuran
4-Methyldibenzofuran
7-Methylbenzofuran
[I1,l'-Biphenyl]-carboxy aldehyde
2-Chloro-l,3,5-cycloheptatriene
Conventional Variables
Grain size
Oil and grease
Sulfides
Total organic carbon
Total volatile solids
12
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eutrophication, microbial contamination, and toxic chemical contamination)
are described below, and further explained in the section "Data Summaries."
It should be noted that these indices are not used in lieu of the original
data (e.g., contaminant concentrations), but in addition to them. The
original data are used to identify and characterize detectable levels of
contaminants and their effects on the environment. The indices are used to
reduce large data sets into interpretable numbers that reflect the relative
magnitudes of the different variables among areas, and thereby aid in the
decision-making process.
Eutrophication
Impacts associated with eutrophication were evaluated based on direct
comparisons of dissolved oxygen concentrations in Budd Inlet with Washington
State water quality standards and with established values below which
biological communities are considered stressed. Dissolved oxygen was
selected to represent eutrophication because oxygen depletion may directly
impact the biota. Nutrient depletion is not know to results in environmental
degradation.
Microbial Contamination
The relative magnitude of fecal coliform bacteria concentrations was
quantified using a simple index. The index is the ratio between the
geometric mean concentration at a site and the water quality standard for
fecal coliform concentrations in that portion of Budd Inlet. The ratio is
structured so that the value of the index increases as the deviation from
the water quality standard increases. The index for fecal coliform bacteria
(FCBI) is expressed as:
where:
FCBI-jj = Index for medium i (i.e., water or shellfish) in area j
13
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= Geometric mean concentration in medium i at Budd Inlet study
area j
ij = Concentration that is the water quality standard for medium i
in Budd Inlet study area j.
Note that regulatory standard for fecal coliform concentrations vary
depending on the medium (i.e., shellfish vs. water) and the state classi-
fication of local waters.
Toxic Chemical Contamination
There were too few data to adequately characterize contaminant
concentrations and biological effects in the water column. Consequently,
contaminant and biological effects indices were only developed for chemical
concentrations in sediments, sediment toxicity bioassays, and bioaccumulation
of chemicals in shellfish.
Sediment Chemistry Indices--
Two kinds of indices were used to characterize concentrations of
chemical contaminants in sediments. Chemical contaminants measured in Budd
Inlet sediments were compared with Puget Sound wide reference conditions
using EAR values. AET values were used to determine the potential toxicity
of chemical concentrations in sediments, and to identify specific chemicals
or compound groups that are of major concern in Budd Inlet.
EAR values for chemical contaminants measured in Budd Inlet were
calculated using the expression:
FAR •• - r •'ir •
trtKsij ~ Lsij/Lsir
where:
EARs-jj = EAR for sediment concentration of chemical i at Budd Inlet
study area j
14
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Csjj = Sediment concentration of chemical i at Budd Inlet study area
j
^sir = Average concentration of chemical i in Carr Inlet reference
sediments.
An EAR value that is greater than 1 indicates that the concentration for a
particular chemical and study area in Budd Inlet exceeded the average
reference concentration for that chemical in Carr Inlet sediments. However,
because sediment chemistry samples are not replicated, statistical com-
parisons between concentrations of chemicals in contaminated areas and those
in the Carr Inlet reference area was not possible. Consequently, the
significance of an EAR value for a given chemical is determined by comparison
with Puget Sound wide reference data. If the concentration of a given
chemical in Budd Inlet sediments is greater than the maximum concentration
for that chemical in all Puget Sound reference areas, the EAR value for
that chemical is judged to be significantly elevated. Thus, it is possible
to have EAR values greater than 1 (i.e., that exceed average Carr Inlet
reference conditions) that are not deemed to be significantly elevated
because they fall with the range of all Puget Sound reference conditions.
AET values have been developed for many Puget Sound contaminants of
concern. AET values are based on sediment chemistry data, toxicity data,
and benthic infauna abundance data for wide number of contaminated sites and
reference areas throughout Puget Sound. For a given chemical and a specified
biological indicator (e.g., amphipod mortality), the AET is the concentration
above which statistically significant biological effects occurred in all
samples of sediments analyzed. Thus, comparison of contaminant concentra-
tions for individual chemicals measured in Budd Inlet sediments with their
corresponding AET values is a means of determining the potential severity of
biological effects in Budd Inlet, and of selecting and prioritizing
chemically contaminated areas for remedial action.
Puget Sound AET values are particularly relevant to the evaluation of
sediment contaminant concentrations and potential biological effects in Budd
Inlet. Specifically, the AET database includes contaminant data from Eagle
Harbor that includes a suite of compounds with high concentrations that are
15
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similar to the compounds with high concentrations in Budd Inlet. This
similarity is probably due to the occurrence of wood treatment facilities on
the shores of both embayments. The AET database contains information on
sediment toxicity and biological effects from areas of low, moderate, and
high sediment contamination, as well as from areas with different kinds of
contamination (e.g., metals and organic substances). Thus, the AET values
integrate a wide range of chemical contaminant and biological effects
information from other Puget Sound studies that can be used to predict
environmental effects and prioritize study areas in Budd Inlet.
Biological Effects Indices--
Biological effects indices for chemical bioaccumulation in shellfish
and for sediment toxicity (i.e., amphipod mortality and oyster larval
abnormality bioassays) were developed using the EAR approach described above.
The analysis of EAR values for contaminant bioaccumulation was limited
to the available data for clams. Bioaccumulation data were not available
for fish or other kinds of shellfish in Budd Inlet. The EAR index for
bioaccumulation was calculated using the expression:
EARtij = ctij/ctir
where:
EARtij = EAR f°r chemical i in tissue t (i.e., shellfish) at Budd
Inlet study area j
Ctl-j = Concentration of chemical i in tissue t at a Budd Inlet
study area j
Cfjr = Concentration of chemical i in tissue t at reference area j.
Determination of the significance of EAR values for bioaccumulation was not
possible because methods for such a determination have not been established.
However, bioaccumulation data were also used to assess potential human
16
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health risks associated with ingestion of contaminated shellfish from Budd
Inlet. Thus, EAR values may be judged significant for those substances and
areas that pose an unacceptably high human health risk that is associated
with ingestion of chemically contaminated shellfish.
EAR analysis for toxicity of Budd Inlet sediments was based on available
data for mortality measured in the amphipod (Rhepoxvnius abronius) sediment
bioassay, and for developmental abnormality measured in the oyster larval
(Crassostrea qiqas) sediment bioassay. The EAR indices for sediment
toxicity are comparable with those for sediment contamination and bioaccumu-
lation, and were calculated using the expression:
ij = Rij/Rir
where:
EAR-jj = EAR for the toxicity response of bioassay species i at Budd
Inlet study area j
R-JJ = Toxicity response of bioassay species i to sediments from
Budd Inlet study area j
R-jr = Toxicity response of bioassay species i to sediments from
reference area r.
Significance of the EAR values was determined by statistical comparisons of
individual bioassay responses to sediments from the study area with response
to sediments from an appropriate reference area.
PROBLEM AREA IDENTIFICATION
As indicated in the foregoing sections, the preponderance-of-evidence
approach used in the decision-making framework is largely based on develop-
ment of indices for contamination and biological effects relative to a
reference site or reference condition. In the action plans developed for
Elliott Bay and Everett Harbor (Tetra Tech 1985b,c), the various contaminant
17
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and biological effects indices were compiled into an action assessment
matrix that could be used to collectively assess the magnitude and spatial
extent of impacts relative to reference conditions. In the Elliott Bay and
Everett Harbor Action Plans, the number and magnitude of the various indices
were used to score and rank potential problem areas.
In the case of Budd Inlet, the development of an action assessment
matrix and a systematic scoring procedure was not feasible because such an
approach is based on the availability of synoptic data for a number of
complementary variables (i.e., chemistry, toxicity, fish histopathology, and
biological communities) as measured at a large number of sites. The Budd
Inlet data are derived from a wide number of studies conducted at various
times during the past 5-10 yr, and which varied considerably in study
objectives, study design, sampling locations, sampling variables, and
analytical methods. Consequently, problem area definition for Budd Inlet
was based on a more general categorization of the contaminant and biological
effects indices.
As shown in Table 3, three priority levels were established depending
on the magnitude of the various indices for each type of pollution problem
(i.e., eutrophication, microbial contamination, and toxic chemical contamin-
ation). Each study area in Budd Inlet was therefore prioritized in terms of
further action, if any, needed to remediate problems associated with
eutrophication, microbial contamination, and toxic chemical contamination.
18
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TABLE 3. CRITERIA FOR PRIORITIZING PROBLEM
AREAS IN BUDD INLET3
No
Data Category Highest Priority Secondary Priority Immediate Action
Eutrophication Minimum dissolved Minimum dissolved Minimum dissolved
oxygen <3.0 mg/L oxygen 3.0-5.0° mg/L oxygen >5.0" mg/L
Toxic
contamination0
Sediment Metals: EAR >50 Metals: EAR 10-50 Metals: EAR <10
chemistry Organics: EAR >100 Organics: EAR 10-100 Organics: EAR <10
Bioassay Amphipod >50% mortality Amphipod 25-50% mortality Amphipod <25% mortality
Oyster >50% mortality Oyster 25-50% mortality Oyster <25% mortality
Microbial Fecal coliform bacteria Fecal coliform bacteria Fecal coliform bacteria
contamination EAR >10 EAR ld-10 EAR
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PHYSICAL SETTING
PROJECT LOCATION
Budd Inlet is a shallow estuary located at the extreme southern end of
Puget Sound (see Figure 1). It includes the area south of a line joining
Cooper Point and Dover Point. The inlet is approximately 6.9 mi long with an
average width of 1.15 mi, and a maximum width of 1.61 mi. The Deschutes
River is the major freshwater source to Budd Inlet and enters the inlet at
its southernmost point. In 1951, Capitol Lake was created when a dam was
constructed over the tidal flats where the Deschutes River empties into Budd
Inlet. Capitol Lake is not considered part of the study area. However, the
Capitol Lake outfall is considered a point source to Budd Inlet. Budd Inlet
is the most developed estuary in southern Puget Sound. Most urban and
industrial activity is located in the Cities of Tumwater and Olympia at the
southern end of the inlet. Much of the remaining shoreline is relatively
undisturbed. Physical oceanography, geological setting, drainage patterns,
climate, land use, and beneficial use are described below.
PHYSICAL OCEANOGRAPHY
Budd Inlet is a partially mixed shallow estuary with muddy substrates.
The average depth of the inlet is 27 ft at mean lower low water (MLLW), and
maximum depth near the mouth is about 110 ft. There is no entrance sill.
The shoreline and intertidal areas are moderately steep. The only inter-
tidal mud flats are located at the southern end of the inlet. They result
largely from sediment deposited by the Deschutes River.
Puget Sound enters Budd Inlet through the Tacoma Narrows and Dana
Passage, and is diluted at the inlet head by the Deschutes River. Water
properties in Budd Inlet reflect these salt water and freshwater sources.
Temperature ranges in Budd Inlet (7-21° C) exceed those in the Puget Sound
main basin (8-18° C). The range of salinity in Budd Inlet (11-31 ppt)
20
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exceeds that of the Puget Sound main basin (23-30 ppt; Oclay 1959). At
times of high runoff, a surface layer of low salinity water is observed
(Oclay 1959).
The circulation pattern in Budd Inlet is a weak two-layered system.
The lower water column flows south toward the head of the inlet, and the
upper water column flows north out of the inlet (URS 1986). URS (1986)
found evidence of a counter-clockwise gyre off Tykle Cove and the eastward
movement of surface water from West Bay to East Bay.
URS (1986) used a field-calibrated box model to estimate the residence
time of water parcels in Budd Inlet. The study area was extended approxi-
mately 1 mi south of Cooper Point to 3/8 mi north of the Port of Olympia
peninsula. Estimates of residence times were not made for the Olympia
Harbor area including East and West Bays. Although the box model assumed a
steady-state net circulation throughout the inlet, those portions of the
inlet most influenced by tidal exchange would have proportionately shorter
residence times. The model estimated that a parcel of water would require
approximately 4 days to travel from near the head of the inlet to near the
mouth, and that the maximum residence time of a parcel entering the inlet
throughout the mouth would be approximately 14 days. The mean residence
time, given variability in circulation and flushing characteristics
throughout the inlet, was estimated to be 8 days.
Dissolved oxygen near the head of Budd Inlet is depleted during late
summer due to a combination of factors including stratification, reduced
flushing rate, and algal blooms. Oxygen values are commonly below the 5.0-
mg/L Washington State Class B water quality criterion south of Priest Point
(Egge, E., 25 January 1987, personal communication; Alan, R., 24 September
1987, personal communication; U.S. EPA, 7 January 1988, personal communica-
tion). Near-bottom oxygen levels may be less than 3.0 mg/L in East and West
Bays.
21
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GEOLOGY
The Budd Inlet region is geologically and topographically similar to
other coastal regions in southern Puget Sound, reflecting the influence of
mountain building and glacial activity. The steep terrain of the upper
Deschutes basin was formed during periods of sediment deposition followed by
uplift and mountain building. The underlying bedrock is therefore volcanic
(basalt and andesite) or sedimentary (sandstone and siltstone). Lowland
areas in the basin are composed of unconsolidated glacio-fluvial materials.
The subsurface layer of glacial outwash mainly consists of unconsolidated
sands and gravels (McNicholas 1984). The porosity of these soils results in
poorly developed drainage patterns in the basin.
The high permeability of the soils also allows for rapid uptake of
winter rainfall thereby recharging an extensive aquifer. Porous soils in
much of the region overlay a shallow substructure of hard pan that is within
40 ft of the surface in some places. Because this shallow hardpan results
in a very shallow aquifer, groundwater is available at relatively shallow
depths. In over 80 percent of the wells, the water level is within 50 ft of
the surface (Arvid Grant and Associates 1973).
The subsurface rock bordering the inlet is heavily fractured and
elevations may vary from 0 to 300 ft above sea level in as little as 2 mi.
These soils consist of a layer of Vashon till overlying an assortment of
glacial deposits (Arvid Grant and Associates 1973).
The intertidal beaches of Budd Inlet are moderately steep. Much of the
subtidal area consists of recent bay muds, fine-grained glacial sand and
silt, and lake sediments. The bay muds are recent deposits of silty organic
clays [U.S. Army Corps of Engineers (COE) 1980]. These are very soft, low
density, and possess a high water content. Muds are replenished by
biodegradation and silts are deposited by the Deschutes River.
The annual sediment load of the Deschutes River is approximately 18,300
tons; 80 to 85 percent is transported during November and December. The
22
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majority of this sediment load originates from the erosion of streambeds and
banks along the mainstem of the river (Moore and Anderson 1979). Capitol
Lake acts as a settling basin for sediment transported by the river. Between
1951 and 1976, Capitol Lake trapped 2 million tons of sands, silts, and clays
eroded from streambanks and slopes in the watershed (McNicholas 1984).
Sedimentation is also a problem in Budd Inlet at the Capitol Lake outfall
and in East Bay, which require dredging by both the Olympia Yacht Club and
the Port of Olympia. The U.S. Army COE conducts maintenance dredging of the
shipping lanes, with the average dredging operation yielding 400,000 yd^ of
sediment, largely of Deschutes River origin (McNicholas 1984).
DRAINAGE PATTERNS
The Budd Inlet drainage area encompasses primarily undeveloped rural and
forest lands in the Deschutes River drainage basin (Figure 4). This
watershed is bound on the east by the Nisqually River Watershed and on the
west by the drainage of the Black River and western Puget Sound. In
addition to the Deschutes River, the basin includes several other small
streams, including Percival and Moxlie Creeks. The drainage pattern of the
basin is not well developed due to the high groundwater storage capabilities
of the soil. During periods of heavy precipitation, the permeability of
surface soils and subsoils results in infiltration and groundwater recharge
rather than overland flow to surface water drainages.
The Deschutes River originates in the Bald Hills and from Cougar
Mountain, flows northwest for 57 mi, and empties into the southern end of
Budd Inlet. The flow regime is typical of the rainfed streams in western
Washington. Peak flows occur in the winter months and may exceed 5,000
ft-Vsec/mo (Arvid Grant and Associates 1973). Minimum flow occurs in the
late fall, typically 66-100 ft^/sec, with average annual flows of 409
ftVsec (Moore and Anderson 1979).
The Deschutes drainage basin encompasses approximately 166 mi2 (McNi-
cholas 1984). The upper portion of the watershed comprises heavily forested
land and rugged terrain. Rural communities and agricultural land dominate
the lower basin. Less than 21 mi2 of the Deschutes basin is urbanized
23
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ro
-F*
BUDD INLET
DRAINAGE BASIN
DESCHUTES RIVER
DRAINAGE BASIN
Pierce County
10
miles
kilometers
Thurston County
Lewis County
10
15
Note: Nisqually River marks the boundary between Thurston and Pierce Counties
Reference: McNicholas (1984).
Figure 4. Budd Inlet and Deschutes River drainage boundaries.
-------
(Arvid Grant and Associates 1973). An additional 59 mi^ drains directly to
Budd Inlet from surrounding slopes.
CLIMATE
Climate in the Budd Inlet region is characterized by mild, wet winters
and warm, dry summers. Daily and seasonal variations in temperature are
relatively small. During the summer, daytime temperatures range from about
70° to upper 80° F and usually ranges from 40° to upper 50° F at night.
Winter temperatures range from about 30° to low 50° F (Arvid Grant and
Associates 1973). Freezing seldom occurs and snowmelt is rarely a signifi-
cant contributor to stream flow or runoff. Severe storms are rare.
Rainfall, accompanied by prolonged cloudy periods, is the dominant
feature during the winter months. Eighty-five percent of the total annual
precipitation occurs from October through April (Arvid Grant and Associates
1973). Most of the precipitation is light to moderate rainfall, occurring
continuously for long periods of time. The summer months are usually dry..
occasionally with no measurable rainfall for periods up to 30 days. While
mean annual precipitation at the Olympia airport is 52 in/yr, precipitation
may be greater at higher elevations (McNicholas 1984).
LAND USE
Historically., the region surrounding Budd Inlet has been largely rural
or undeveloped. Industrial and urban activities are concentrated at the
southern end of the inlet in the Olympia and Tumwater area. Many areas in
this vicinity are sites of greatly increased growth and development. For
example, in the Percival Creek basin, employment increased 2,870 percent
from 1970 to 1980, and the population increased 255 percent (Thurston
Regional Planning Council 1985). This urbanization of the watershed is
cited as the probable cause of increased streamflow and runoff to Percival
Creek (McNicholas 1984). Similarly, land use changes resulting in decreased
natural vegetation are expected to increase storm drainage problems, while
population increases will result in greater demands on sewage and septic
systems.
25
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The Cities of Lacey, Olympia, and Tumwater possess the only formal
sewage collection systems in the basin. All of these cities use the LOTT
WWTP for final treatment and discharge into Budd Inlet. The central
business district and older areas of Olympia are served by both a sanitary
and storm sewer system. The sanitary sewer systems feed into the LOTT WWTP
and storm sewers discharge directly into Budd Inlet. There are two CSOs
that divert peak flows past the LOTT WWTP and directly into Budd Inlet.
Specific information on the LOTT WWTP is provided in the third section
entitled Contaminant Sources.
In rural and less-developed areas of the basin, sewage is generally
discharged into septic tanks and leaching fields. The efficiency of these
systems depends to a large degree on the ability of the soil to absorb the
waste material. Over two-thirds of the area is considered to have severe
soil limitations due to poor drainage (An/id Grant and Associates 1973).
Much of the rural area of the basin has no problem with septic tank usage,
but problems are apparent in localized areas due to both soil characteristics
and population densities (e.g., Cooper Point and Summit Lake). If the
present trend of increased development and growth continues, problems with
septic tank usage are expected to increase.
BENEFICIAL USE
Budd Inlet is used for a variety of purposes ranging from marine
transportation to salmon rearing, and from beach combing to boating. In the
context of this study, the term "beneficial use" refers to activities that
depend on a high degree of environmental quality and that do not, as a
direct consequence, adversely affect that quality. Beneficial uses can be
placed into two categories: 1) resource using, and 2) nonresource using.
Resource-using activities include shellfish harvesting and fishing.
Nonresource-using activities include scuba diving, beach combing, and
recreational boating.
Fish and shellfish are important resources in Budd Inlet. Five species
of anadromous fish spawn in the Deschutes basin: Chinook, coho, and chum
26
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salmon; sea-run cutthroat; and steelhead trout (U.S. Army COE 1980). The
Washington Department of Fisheries manages an extensive salmon propagation
program in Capitol Lake. Other fish species harvested recreationally in
Budd Inlet include cod, surf perch, sole, flounder, and herring. Surf smelt
spawn on the beaches around the inlet.
In 1987, Ecology issued an advisory notice recommending that shellfish
from lower Budd Inlet not be consumed or harvested (Bradley, D., 12 January
1987, personal communication). That recommendation was based on the
following factors:
• Concentrations of polycyclic aromatic hydrocarbons (PAH) in
clams from near the Cascade Pole Company in southern Budd
Inlet are significantly higher than concentrations in clams
from less-contaminated areas in the Puget Sound region and
are similar to those reported in clams from Eagle Harbor
• Based on procedures developed for the Puget Sound Estuary
Program (PSEP) (Tetra Tech 1986a), it appears that long-term
consumption of shellfish with concentrations of PAH similar
to those reported in clams from Budd Inlet represents a
significant health risk.
Individual lifetime carcinogenic risks associated with the ingestion of
these contaminated shellfish range from l.SxlO"4 to 1.5x10 (Bradley, D.,
12 January 1987, personal communication). These levels exceed the 1x10"
lifetime risk level that is often used as a reference point for the
management and regulation of carcinogenic chemicals. A range of PAH
concentrations in shellfish (i.e., 278-940 ug/kg wet weight) and additional
assumptions concerning exposure duration (35 yr) and seafood ingestion rates
were used to generate risk estimates (Bradley, D.f 12 January 1987, personal
communication).
27
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DATA SUMMARIES
CONTAMINANT SOURCES
Contaminant sources in the study area can be divided into six major
categories: wastewater treatment plants (WWTP), combined sewer overflows
(CSOs), surface runoff, industrial sources, groundwater, and accidental
spills. There are four WWTP in the study area: Tamoshan Development/Thurs-
ton County Public Works, Beverly Beach Utilities Association, Seashore Villa
Mobile Home Park, and LOTT (for Lacey, Olympia, Tumwater, and Thurston
County) (Figure 5). During storm events, untreated wastewater overflows
from city combined sewer lines through two CSO outfalls in Olympia. Surface
runoff originates from excess precipitation draining from the land surface.
This runoff is discharged to Budd Inlet from storm drains, natural drainage
channels, and direct surface runoff. Groundwater includes any subsurface
transport of contaminants into the inlet. Industrial discharges comprise
permitted discharges of wastewater and storm water, and unpermitted (e.g.,
storm drains) discharges of storm water from individual industrial sites.
The accidental spills category includes those contaminants that are released
to Budd Inlet from spills in the study area. A more detailed description of
these six categories of contaminant sources is provided below.
Wastewater Treatment Plants
Effluent limitations are shown in Table 4 for each of the four WWTP
named above. These WWTP are permitted under the Clean Water Act, Section
301(h) National Pollutant Discharge Elimination System (NPDES). Although
Shorewood Estates operates a treatment plant, this facility does not have an
NPDES permit because it discharges to a drainfield.
28
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INDUSTRIAL
PETBOLEUM
DISTRBUTORS
OIL-CONTAMINATED SOLS
(EARTH CONSULTANTS.
7 AUGUST 1666, PERSONAL
COMMUNICATION]
PAST TEXACO BULK
PETROLEUM STORAGE
FACILITY
MC FAFLANOCASCADE
HARDEL
HISTORICAL LANDRLL
•
= UN1NVESTTGATED
POTE MTIAL SOURC ES
OF FECAL COLJFOHM
BACTERIA
= NPOES-PERMfTTED
DISCHARGES (SEE
TABLE 6)
= MARINA
LOCATIONS OF AREAS WHERE
CONTAMINATED SEDIMENTS
WERE IDENTIFIED PRIOR
TO DREDGING
(T) = US. ARMY COE (NO DATE (C)]
(2) = US ARMYCO£[NODATE(D})
(3) - U.S ARMYCOEfNODATEfK)]
OLYMPIA
CITY
BOUNDARY
Ir-,
OLYMPIA
Figure 5. Locations ol potential point and nonpolnt discharges
of contaminants to Budd Inlet.
-------
TABLE 4. LIST OF NPOES-PERHITTED WASTE DISCHARGES TO BUDD INLET
Facility
Cascade Pole Co.
Chevron U.S.A., Inc.
Oelson Limber, Inc./
Olympia Forest
Products Co., Inc.
Beverly Beach
Utilities Association
O city of Olympia/LOTT
Seashore Villa Mobile
Home Park
Tamoshan Development/
Thurston County
Public Works
Facility Description
Wood treatment
Bulk petroleum storage
Lumber mill
Secondary WWTP
Regional secondary WWTP
Secondary WWTP
Secondary WWTP
Effluent Limitations3
See Comments
15 mg/L 0 & GE
15 mg/L 0 & G
Minimum contribution of
solids (e.g., chips, wood
debris) from site
30 mg/L (1.25 Ib/day) BOD
30 mg/L (1.25 Ib/day) SS
20/100 mL fecal coliform
bacteria
Outfalls 1-2: 16.3 MGD
30 mg/L (4,000 Ib/day) BOD
30 mg/L (4,000 Ib/day) SS
200/100 mL fecal coliform
bacteria
0.015 MGD
30 mg/L (3.8 Ib/day) BOD
30 mg/L (3.8 Ib/day) SS
200/100 mL fecal coliform
bacteria
0.035 MGD
30 mg/L (916 Ib/day) BOD
30 mg/L (916 Ib/day) SS
200/100 mL fecal coliform
bacteria
Comments
Permit for stormwater runoff discharge expired 7 November 1985.
Facility closed prior to 13 March 1987. Ecology maintains that
product is currently discharging from the site, and that the
discharge should be permitted (Peeler, M., 12 January 1988,
personal communication).
Stormwater runoff from truck loading area and building roof drains
routed to oil-water separator. Automatic pump from separator
discharges effluent into storm drain. Permit expires 25 June 1990
(Ecology 1985a).
Stormwater runoff. Permit is in effect only when facility is in
operation. Permit expires 16 December 1990 (Ecology 1985b).
Average flow is <3,000 gal/day. Approximately 18 homes are
connected to the WWTP. Permit expires 28 August 1990 (Ecology
1980).
Existing design capacity limited to 22 MGD (maximum average wet-
weather flow). WWTP online August 1982. Permit expires 25
September 1992 (Ecology 1987).
Average flow is 3,600 gal/day. Permit expires 25 May 1989 (Ecology
1979).
Seventy-four residences in development. Discharge monitoring
reports from January 1982 to December 1985 indicate problems with
meeting effluent limitations for SS and fecal coliform bacteria.
Permit expires 20 October 1991 (Ecology 1986).
a Effluent limitations are listed as monthly averages for wastewater treatment plants (WWTPs) and daily averages for other permits, unless otherwise noted. All
discharges into Budd Inlet must be within pH 6-9. All WWTPs must also meet permit requirements for residual chlorine. OSG = oil and grease, BOD = 5-day biochemical
oxygen demand, SS = suspended solids.
b Daily maximum efflu- nt limitation.
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LOTT WWTP--
The LOTT treatment plant is located on City of Olympia property in the
southern portion of Budd Inlet (see Figure 5). This regional facility
services portions of the Cities of Lacey, Olympia, and Tumwater, and
Thurston County. In August 1982, the LOTT plant was upgraded to provide
secondary treatment of municipal and industrial wastewater. The most
current information listed the average wet-weather flow as approximately 11
MGD (Parametrix 1987c). Based on effluent requirements in the NPDES permit
(Ecology 1987), the monthly average flow is limited to 16.3 MGD, and the
design criteria for the plant are 11.8 MGD (monthly average dry-weather
flow), 16.3 MGD (monthly average wet-weather flow), and 25.9 MGD (maximum
daily flow). Upon completion of certain hydraulic and other improvements,
the plant has an existing design capacity of 22 MGD (average daily flow), 27
MGD (maximum daily flow), and 35 MGD (peak flow) (Parametrix 1987b).
The LOTT plant currently discharges treated effluent to Budd Inlet via
a 30-in diameter principal outfall and a 48-in diameter backup outfall (see
Figure 6). The 30-in diameter principal outfall line extends past the
northern tip of Washington Street with an additional 600 ft of submerged
line and a 300-ft diffuser section. The 48-in diameter backup outfall
discharges through an open-ended pipe into the Fiddlehead Marina area.
Prior to construction of the 30-in diameter principal outfall, LOTT dis-
charged primary-treated effluent via the 48-in diameter outfall, which
extended about 100 yd offshore (Alan, R., 19 January 1988, personal com-
munication). The 48-in diameter outfall currently serves as a backup line
to handle flows that exceed the capacity of the 30-in diameter principal
outfall (i.e., flows of >10-12 MGD; Alan, R.( 19 January 1988, personal
communication). All effluent is treated before it is discharged from this
outfall. Because of plant hydraulics and the need to use the chlorination
units for disinfection, the 48-in diameter backup outfall is used several
times each day (Ecology 1987). The calculation of the actual volume of
effluent diverted and discharged through the 48-in outfall at any given
tidal height is not possible at this time (URS 1986). However, by overlaying
tidal cycles upon LOTT discharge flows, URS determined the volume of
effluent discharged during two sampling periods. During a 5-day period in
31
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PRIEST
\ VPOINT
30" CSO
(WATER
-iSTREET)
CAPITOL
LAKE
^30" SAN FRANCISCO
, STORM SEWER
48" CSO
(STATE AND
CHESNUT"
STREETS)
4 in TO 19 In STORM DRAIN OUTFALLS
24 In TO 29 In STORM DRAIN OUTFALLS
> 30 in STORM DRAIN OUTFALLS
Figure 6. Locations of storm drain outfalls in Budd Inlet.
32
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September 1984, four events of 7-8 MGD and two events of 4-6 MGD occurred.
During a 5-day period in May 1985, two events of 9-12 MGD, three events of
7-8 MGD, and two events of 4-6 MGD occurred. Mr. R. Alan (25 March 1988,
personal communication) stated that there are currently no annual or monthly
estimates of the volume of effluent that is discharged via the 48-in
diameter outfall. Mr. R. Alan estimated that approximately 10-20 percent of
LOTT's daily flow is discharged via the 48-in outfall. Future plans include
the elimination of the 48-in diameter backup outfall during the expansion of
i
the LOTT facility (Parametrix 1987a). This expansion is planned to occur
within the next 2-3 yr (Alan, R., 25 March 1988, personal communication).
According to Mr. R. Alan, LOTT plans to build a second 30-in diameter
outfall parallel to the existing 30-in diameter outfall. Future plans at
LOTT also include nutrient removal from the effluent, which is a form of
advanced or tertiary wastewater treatment (Colby, T., 28 March 1988,
personal communication).
The LOTT collection system is largely a separate sanitary sewer system.
However, a portion of the downtown Olympia system is combined with the storm
sewer system and impacts peak storm flows to the WWTP. Various commercial
and small industrial flows also enter the collection system. URS (1980)
completed an industrial waste survey for the City of Olympia, in which they
identified commercial industrial users that discharge or have the potential
to discharge liquid and solid wastes to the municipal sewer system. Thirty-
four of the 37 industries that were contacted responded to URS's question-
naire. Nineteen of those 34 industries discharged process water to the
municipal WWTP. Prior to URS's survey, U.S. EPA indicated that in 1976
national categorical pretreatment standards would be issued for 21 types of
industries that were potentially capable of discharging priority pollutants
to WWTP. Those industries have been referred to as primary industries. In
the URS (1980) survey, seven of the 19 industries that discharged to the
municipal WWTP were primary industries. Those seven industries are Hardel
Mutual Plywood Corporation, D.G. Parrott & Son, Star Cleaners & Foundry,
Ann's Car Wash, Jerry's Shell Service, Olympia Auto Detailing, and Rich's
Auto Detailing.
33
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In addition to those seven industries, URS (1980) identified other
industries that discharged potentially contaminated wastewater to the
municipal WWTP. Survey responses indicated that wastewater from the Olympia
Brewing Company may have exhibited excessive pH, temperature, 5-day
biochemical oxygen demand (8005), and suspended solids, and that they may
have contained halomethanes. According to Ecology (1987), the Olympia
Brewery is the only major industrial impact to the LOTT WWTP. Currently..
the brewery discharges up to 2 MGD of effluent, 21,000 Ib/day of 6005, and
pH ranges from 6 to 10. Ecology (1987) data indicate that in recent years
the brewery has occasionally violated the pH limits, which substantiates
results from the URS (1980) survey. Olympia Brewery's permit has expired
and a new permit application is under review by Ecology.
Survey responses from URS (1980) also indicated that the Olympia
Medical Laboratory process wastes may have contained concentrations of
chromium, nitrophenols, and cyanide. Wastewater discharged to the sewer
system from St. Peter Hospital may have contained mercury, benzene, chlorina-
ted naphthalenes, chloroform, and phenols. Process wastes from two radiator
shops in the survey area may have contained concentrations of antimony,
lead, zinc, and copper.
Although few priority pollutants were identified from survey results,
URS (1980) recommended that a general scan for priority pollutants in
influent and effluent wastewater at the treatment facility should be
conducted to characterize system wastewater. This information would also
be used to implement an industrial pretreatment program for the current LOTT
WWTP. Currently, the LOTT WWTP does not have a pretreatment program. Each
governmental entity regulates discharges into their portions of the
collection system. Under the new NPDES permit (Ecology 1987), a pretreatment
interjurisdictional agreement must be developed and implemented by 1 April
1988, and an industrial waste survey must be completed by 30 September 1988.
Parametrix (1987c) has recently prepared a draft environmental impact
statement for the LOTT Urban Area Wastewater Management Plan. This plan
will provide a comprehensive regional program for wastewater collection,
treatment, disposal, and management, and a discussion on the protection of
34
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the area's aquifers. The plan addresses the development of an interceptor
system for wastewater collection, and improvements to the treatment and
disposal system at the existing LOTT facility.
Tamoshan WWTP--
The Tamoshan WWTP is located approximately 5 mi north of downtown
Olympia on the Cooper Point peninsula (see Figure 5). The facility provides
secondary municipal treatment for wastewater from the residential community
of Tamoshan. This development consists of approximately 74 residences
(Ecology 1986) with a population of approximately 140 persons (Clark, D., 27
January 1986, personal communication). A review of 1980 discharge monitoring
reports (DMRs) showed an average discharge of 0.0134 + 0.0009 MGD (Determan,
T., 19 February 1981, personal communication) and a review of 1983 DMRs
showed a yearly average discharge of 0.018 MGD (URS 1986). According to the
NPDES permit (Ecology 1986), the monthly average quantity of effluent
discharged shall not exceed 0.035 MGD. Because the facility does not have a
flow meter, its wastewater flows are estimated based on the number of sump
pump cycles/day and sump volume. According to DMRs for 1983, flow from the
Tamoshan facility account for loadings of 3.0 Ib/day total nitrogen and 0.8
Ib/day total phosphorous to Budd Inlet (URS 1986).
At the Tamoshan facility, chlorinated effluent is collected in a wet
well. When the well becomes full, effluent is pumped into the outfall line.
As a result, the discharges into Budd Inlet are intermittent (Kendra, W. and
T. Determan, 6 November 1985, personal communication). Effluent is
reportedly discharged to Budd Inlet via a pipe with a length of 738 ft
(Kendra, W. and T. Determan, 6 November 1985, personal communication).
Although conflicting information is presented by Mr. D. Clark (27 January
1986, personal communication) (i.e., a 1,500 ft 6-in pipe) and Mr. T.
Determan (19 February 1981, personal communication) (i.e., a 328-ft pipe),
Mr. D. Anderson (6 April 1988, personal communication) indicated that the
pipe is approximately 740 ft. Based on dye studies, the high density and
compact nature of the emergent dye patch suggests lack of a diffuser
(Kendra, W. and T. Determan, 6 November 1985, personal communication).
35
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Tamoshan DMRs from November 1979 through November 1980 showed fecal
coliform bacteria arithmetic averages ranging from 43 to 67,000 counts/100
ml (Determan, T., 19 February 1981, personal communication). Seven of nine
DMRs indicated that fecal coliform bacteria levels in samples collected
inside the plant violated effluent limitations. However, the expected fecal
coliform bacteria levels at the actual discharge point or in the dilution
zone adjacent to the diffuser could not be determined due to the lack of
data. The DMRs from January 1982 to December 1985 indicate that Tamoshan's
discharge exceeded effluent limitations for suspended solids and fecal
coliform bacteria. During a limited Class II inspection of this facility in
1985, two fecal coliform bacteria samples exceeded both the monthly and
weekly average for NPDES permit effluent limitations (Clark, D., 27 January
1986, personal communication). High fecal coliform bacteria levels were
also observed in the nearshore areas of the facility. The DMRs suggest that
fecal coliform bacteria contamination of Tamoshan nearshore waters is an
historic and recurring problem. Ecology initially suggested that broken
lines or a small stream located near the facility may have contributed to
these high concentrations of fecal coliform bacteria (Kendra, W. and T.
Determan, 6 November 1985, personal communication). However, the inadequate
disposal of domestic wastes by shoreside residences was later identified as
the most likely source. Ecology concluded that the Tamoshan WWTP does not
appear to be the source of the high counts of fecal coliform bacteria and
that it has little impact on receiving water quality (Kendra, W. and T.
Determan, 6 November 1985, personal communication). However, because
effluent discharge is intermittent, dilution and dispersion of the effluent
plume may not have been fully characterized.
Beverly Beach WWTP--
The Beverly Beach community, which is located approximately 0.4 mi
south of Tamoshan (see Figure 5) and comprises approximately 18 homes
(Ecology 1980). The Beverly Beach WWTP provides secondary wastewater
treatment for approximately 50 persons (Clark, D., 21 November 1985,
personal communication). Although the plant is designed to treat about
5,000 gal/day, the flow is estimated at less than 3,000 gal/day (Ecology
1980; URS 1986). Because the facility does not have a flow meter, wastewater
36
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flows from the facility are estimated based on the resident population
served. Also, although effluent is discharged continuously from the Beverly
Beach WWTP, the discharges are characterized by periodic flow surges that
coincide with plant aeration cycles (Kendra, W. and T. Determan, 6 November
1985, personal communication). According to 1983 DMRs, average loadings of
0.5 Ib/day total nitrogen and 0.13 Ib/day total phosphorous entered Budd
Inlet from the Beverly Beach WWTP discharge (URS 1986). The effluent
discharges through a 6-in gravity-fed line approximately 2 m offshore at a
depth of 0.25 m at mean lower low water (MLLW) (Clark, D.( 21 November 1985,
personal communication). During low tides, the treated effluent discharges
above MLLW and flows down the beach to the receiving water.
During a limited Class II inspection of this facility in June 1985,
samples analyzed for 6005 and fecal coliform bacteria exceeded the NPDES
weekly and monthly average effluent permit limits (Clark, D., 21 November
1985, personal communication)- Ecology concluded that sanitary problems at
the Beverly Beach facility are caused by sporadic chlorination inefficiency
and the shallow depth of discharge. Ecology determined that the Beverly
Beach discharge affects the receiving waters because the initial dilution of
the effluent discharge is minimal due to shallow discharge depth, and the
chlorination efficiency of the WWTP is inadequate during flow surges
(Kendra, W. and T. Determan, 6 November 1985, personal communication).
Seashore Villa WWTP--
The Seashore Villa Mobile Home Park is located between Priest Point and
Gull Harbor on the east side of Budd Inlet (see Figure 5). The Seashore
Villa WWTP services wastewater from over 50 mobile homes and a population of
approximately 174 persons (Clark, D., 25 March 1986, personal communication).
According to the NPDES permit, the monthly average quantity of effluent
discharged is not to exceed 0.015 MGD (Ecology 1979), which is equivalent to
the flow based on the design capacity of the plant. In 1979, Ecology (1979)
estimated that the average flow was 0.0036 MGD, and in 1986 the flow was
estimated to be 0.0115 MGD (Clark, D., 25 March 1986, personal communi-
cation). According to DMRs from 1983, the Seashore Villa WWTP contributed
37
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loadings of 2.5 Ib/day total nitrogen and 0.6 Ib/day total phosphorous to
Budd Inlet (URS 1986).
The Seashore Villa WWTP effluent discharges to Budd Inlet through a
275-yd, 3-in diameter pipe. During a Class II inspection in July 1985, the
depth of the discharge was 2 m at MLLW (Kendra, W. and T. Determan, 6
November 1985, personal communication). Measurements of 6005 and total
suspended solids in effluent samples exceeded the NPDES permit limits, and
Mr. D. Clark (25 March 1986, personal communication) concluded that the
facility did not appear to meet NPDES permit requirements. However, Ecology
also indicated that effluent discharged from Seashore Villa had little or no
effect in the discharge zone (Kendra, W. and T. Determan, 6 November 1985,
personal communication). Fecal coliform bacteria were virtually absent from
surface waters in the mixing zone at Seashore Villa. Seven of 10 samples
collected had fewer than 1 organism/100 ml. However, Ecology stated that
the presence of an algal bloom during the survey may have masked effluent
impacts.
Areas Not Serviced by WWTP--For many years, the Boston Harbor area
(see Figure 5) has been plagued by failing septic systems due to poor soil
conditions. Boston Harbor has reportedly experienced septic system failures
at more than three times the second highest surveyed septic system failure
rate in Thurston County, and more than eight times the rate of failures in
other similar shoreline areas (R.W. Beck and Associates 1986). In April
1984, the Thurston County Public Works, Planning, and Health Departments
conducted a survey of the operational condition of the septic systems in the
Boston Harbor area. Over 68 percent of the septic systems were determined
questionable or failing. Data collected in this study show that failing
drainfield systems are predominant, and that increasing concentrations of
septic wastes are discharged into the area's ditches and marine waters (R.W.
Beck and Associates 1986). The Boston Harbor Wastewater Facilities Planning
Study for Thurston County (R.W. Beck and Associates 1986) was prepared to
assess means of handling septic wastes discharged to Boston Harbor. One
option will likely include the construction of a secondary WWTP.
38
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The Thurston County Health Department identified the following three
unconfirmed areas that may have onsite sewage disposal problems and thus be
sources of fecal coliform bacteria to Budd Inlet: Athens Beach, the French
Loop Road area, and the Olympic Country and Golf Club (Gibbs, T., 20 January
1988, personal communication). The Olympia Country and Golf Club has a
drainfield on the west side of Cooper Point Road that services their
facilities, and possibly some local residences. Wastewater flows downhill
to a collection site and is pumped uphill to the drainfield. The wastewater
in the drainfield reportedly does not flow into Budd Inlet (Haggerty, K.( 18
January 1988, personal communication).
Combined Sewer Overflows
Flows to CSOs result from an overflow of the combined sanitary and
storm sewer system. During a heavy rain storm, additional flow from storm
runoff exceeds the hydraulic capacity of the collection system. The excess
flow, a mixture of storm runoff and raw sewage, is discharged from CSO
discharge points into surrounding waters. With the exception of two known
CSO discharge points, the City of Olympia has separated all storm and sewer
lines in the study area (Moore, D., 17 November 1987, personal communica-
tion). The first CSO is a 48-in diameter outfall that enters a 72-in pipe
approximately 100 ft south of East Bay near State and Chestnut Streets (Alan,
R., 25 March 1988, personal communication). This 72-in diameter pipe
subsequently flows into an 84-in diameter pipe that contains flow from both
Moxlie and Indian Creeks (Moore, D., 29 March 1988, personal communication).
The terminus of the 84-in diameter pipe discharges into East Bay. The second
CSO is a 30-in diameter outfall that enters West Bay near Water Street (see
Figure 6) (Moore, D., 9 December 1987, personal communication). The City
of Olympia is currently preparing a CSO reduction plan, the draft of which
will be submitted to Ecology by 31 July 1988 (Moore, D., 9 December 1987,
personal communication).
These CSOs have not been monitored for flow or chemical composition, and
their flow frequency is unknown (Cunningham, J., 21 September 1987, personal
communication; Alan, R., 25 March 1988, personal communication). The CSO
that enters East Bay via Moxlie Creek may not flow more than once per year
39
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(O'Brien, E., 12 November 1987, personal communication). Mr. R. Alan (25
March 1988, personal communication) stated that neither CSO discharged in
1987 or 1988. Since 1987, LOTT employees visually check the CSOs for flow
when high waters cause the overflow alarms to sound.
Prior to March 1988, untreated sanitary sewage could also enter Budd
Inlet via emergency overflows (EOF). Discharges from EOF are not associated
with a storm event, but result from an equipment fai.lure or a power failure.
EOF are generally located at lift stations to discharge excess flow if the
pump fails. Prior to March 1988, the LOTT facility had two EOF that
discharged into Budd Inlet: the West Bay pump station (2200 West Bay Drive)
and the East Bay pump station (1621 East Bay Drive). The Jasper and
Eastside pump station (1208 Eastside Street) discharged into Mission Creek.
The locations of these pumping stations are shown in Figure 5. According to
Mr. R. Alan (25 March 1988, personal communication), these overflows have
been eliminated. Two EOF were plugged, and a manual valve replaced the
existing automatic overflow at the West Bay pump station.
Surface Runoff
Storm water runoff has long been suspected as a potential source of
pollution to the marine environment. Recently, it has received more
attention as the problems of toxic input from urban runoff have been
recognized. Because a large portion of the study area's drainage basin is
rural and agricultural, the City of Olympia has the only storm drain system.
Over 80 percent of the surface runoff from the study area flows into Budd
Inlet via natural drainage channels (e.g., streams, creeks). Surface runoff
also enters Budd Inlet from the Deschutes River and Capitol Lake.
Surface storm water runoff that occurs within the City of Olympia
boundaries is primarily collected by the city storm sewer system. City
storm drains that discharge directly to Budd Inlet are shown in Figure 6
(City of Olympia 1987; McCarthy, B., 15 January 1988, personal communi-
cation). Within City of Olympia boundaries, surface runoff can also be
collected in the municipal combined sewer system and then treated at LOTT.
40
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Storm water can also discharge to Budd Inlet via natural drainage channels
and as disperse surface runoff.
Storm drain flow was not calculated because information on the size and
land use of the contributing area was not known for each storm drain. There
are essentially no data available to characterize storm drain discharges.
Between 9 and 17 April 1985, URS (1986) estimated flows from 34 pipes,
culverts, and storm drain outfalls that discharge into Budd Inlet. Flow
rates were measured with a Pygmy current meter, and estimates ranged from 0
to 0.284 cubic ft per second (cfs). Flow from the San Francisco storm drain
was between 0.02 and 0.025 cfs. On 10 September 1985, flow estimates from 15
storm water discharges ranged from 0 to 1.203 cfs. Flow from the San
Francisco storm drain was estimated at 0.01 cfs. URS (1986) also intended
to use data collected from the San Francisco storm drain outfall (see Figure
6) to be representative of urban runoff for determination of loadings to Budd
Inlet. However, because the lack of rainfall during the source survey
resulted in very low loadings of 6005, fecal coliform bacteria, dissolved
oxygen, and algal nutrients, these data could not be extrapolated to
represent total urban runoff under more normal wet-weather conditions (URS
1986).
Private industries along the shore of Budd Inlet may also have storm
drain systems that discharge into Budd Inlet. These storm drains were not
characterized as part of this study, but are discussed below in the section
on point discharges to Budd Inlet.
Industrial Sources
Industrial sources can be divided into point and nonpoint sources.
Point sources consist of discrete discharges from an identifiable source.
They are composed primarily of NPDES-permitted discharges and unpermitted
industrial storm drains. The nonpoint sources include any offsite migration
of contaminants resulting from contaminant storage, treatment, and handling
practices. The potential contaminant sources that were identified in the
project area are shown in Figure 5.
41
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Point Sources--
Permitted D1scharQes--Eco1oQv is responsible for issuing NPDES permits.
Ecology statewide policy limits industrial discharges to noncontact cooling
water and storm water. A list of the six existing NPDES-permitted waste
discharges to Budd Inlet is presented in Table 4. Permits have been issued
to four WWTP (i.e., Tamoshan, LOTT, Beverly Beach, and Seashore Villa).
Permits for storm water runoff have been issued to two industries (i.e.,
Chevron and Del son Lumber Company/Olympia Forest Products). Although an
NPDES permit does not currently exist for the Cascade Pole Company site,
Ecology maintains that organic contaminants are currently discharged from
the site and that the discharge requires an NPDES permit (Peeler, M., 12
January 1988, personal communication). Information on discharges from the
four NPDES-permitted WWTP discharges is provided in the previous section
entitled "Wastewater Treatment Plants." Information on discharges from the
Chevron facility and Olympia Forest Products is provided below. Discharges
from the Cascade Pole Company are discussed in the section entitled
"Unpemn'tted Discharges."
Chevron U.S.A. operates a bulk petroleum storage facility near the Port
of Olympia on private property. As identified by Ecology (1985a), the
discharge from this facility consists of storm water collected from the truck
loading areas and building roof drains. This discharge is routed to an oil-
water separator that is located in a bermed area. The oil is drawn from the
separator and discharged into an adjacent buried tank. Waste oils are
pumped from the tank yearly, and hauled to Tacoma by the pumping contractor.
An automatically operated pump discharges effluent into the storm sewer.
Thus, the effluent consists of an irregular and undetermined amount of
storm water discharge.
As identified by Ecology (1985b), Delson Lumber Company/Olympia Forest
Products owns and operates a saw mill and log storage pond on the west shore
of Budd Inlet. This facility discharges undetermined quantities of accumu-
lated storm water and, occasionally, washdown water directly into Budd
Inlet.
42
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Unpernritted Discharges--Industries along the shoreline of Budd Inlet
are served by unpermitted private storm drains that discharge directly to
marine waters. Although flows from these storm drains should be relatively
small, the potential for contamination due to industrial practices could
make private storm drains a significant source of contaminants. U.S. EPA
and Ecology are currently addressing this issue by including industrial
storm drains in the NPDES program.
In the Budd Inlet study area, the locations of most industrial storm
drains have never been defined. Within the study boundaries, the Port of
Olympia operates the largest area serviced by a private storm drain system
[see Port of Olympia (29 February 1988, personal communication) for current
lessees]. The types of operations conducted by lessees and the locations of
the Port of Olympia private storm drains have not been identified. However,
two storm drain outfalls (i.e., West Bay drain outfall and the former
Cascade Pole NPDES-permitted outfall) on Port of Olympia property have been
identified as potential contaminant sources. According to Ecology (Norton,
D., 5 February 1986, personal communication), the West Bay drain is the
major storm water discharge point for runoff from the northern portion of
the Port of Olympia property. This drain also receives storm water collected
along Capitol Way in downtown Olympia. Contaminated groundwater beneath the
Cascade Pole Company facility, located east of the West Bay drain, may also
flow into this drainage system. Recent studies have shown that the former
Cascade Pole NPDES-permitted outfall contributes contaminants to Budd Inlet.
Data on concentrations of contaminants in water and sediments collected near
the West Bay drain and Cascade Pole facility are presented below. Additional
information on results of chemical analyses on sediments collected near the
Cascade Pole outfall are presented in the section entitled "Sediment
Contamination."
Available Data—On 13 February 1985, Ecology collected water samples
from Cascade Pole's former NPDES-permitted outfall and the West Bay drain
(Johnson, A., 22 July 1985, personal communication; Norton, D., 5 February
1986, personal communication). The West Bay drain was resampled on 14
August 1985. In the sample collected from the Cascade Pole outfall, 10 ug/L
of total PAH and 1,700 ug/L of pentachlorophenol (PCP) were detected. In
43
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the sample collected in February from the West Bay drain, 395 ug/L of PAH
and 17 ug/L of PCP were detected. In the sample collected in August from
the West Bay drain, 56 ug/L of PAH and 11 ug/L of PCP were detected. Low
molecular weight PAH (LPAH) accounted for 80 and 85 percent of the total
PAH in the February and August 1985 samples, respectively. High concen-
trations of LPAH is attributed to the predominance of these compounds in
creosote, and because these compounds are more water soluble than high
molecular weight PAH (HPAH). Lower concentrations of LPAH in August may
have resulted from tidal influence at the sampling location. The specific
conductivity of the water sample was 15,500 umhos/cm, suggesting that the
sample was primarily seawater (Norton, D., 5 February 1986, personal
communication). Ecology calculated a 20 Ib/yr flux of PCP to Budd Inlet
from the Cascade Pole Company outfall. Ecology calculated a 300 Ib/yr flux
of PCP from the West Bay drain based on the February 1985 results and 30
Ib/yr flux based on the August 1985 results. Ecology concluded that because
seawater was present in the sewer lines, the actual loads to Budd Inlet may
be lower than these values.
In July 1985, Applied Geotechnology (1986a) collected surface water
samples from standing water in the Port Detention Basin (PDB) and from the
Cascade Pole outfall. Samples were analyzed for PAH and phenols. Results
of these investigations showed no detectable PAH in the PDB or the outfall
sample. Phenols were not detected in water from the PDB. Concentrations of
PCP were detected at 27 ug/L in the Cascade Pole outfall sample. Differences
between results from Ecology and Applied Geotechnology (1986a) may be due
to seasonal effects, tidal effects, variations in sampling or analytical
laboratory procedures, or a change in discharge quality caused by plant
activities. Applied Geotechnology and Ecology concluded that additional
sampling efforts should be conducted to characterize the storm-water system.
In March or April 1988, Ecology will be sampling and tracing the West Bay
storm drain system (Peeler, M., 22 February 1988, personal communication).
Sediment samples will be collected from eight manholes and six catch basins
to determine the connection between the Cascade Pole site and the West Bay
drain outfall.
44
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Nonpoint Sources--
The nonpoint source category includes all other potential indirect
sources of pollution. Offsite migration of contaminants can occur when
surface runoff picks up contaminants as it moves across a contaminated area
of the property, or when contaminants percolate into the groundwater system
where they can be transported to the waterways via groundwater flow.
Groundwater data are presented in the following section. Potential toxic and
microbial contamination from other nonpoint sources is discussed below.
Landfills—Historical landfills may also have contributed contaminants
to Budd Inlet. During construction of the LOTT WWTP, an old landfill was
observed in the area in which the secondary clarifiers were built (Oblas,
V., 29 February 1988, personal communication). The landfill was used prior
to 1950 as a general municipal dump and apparently was operated by the City
of Olympia (Alan, R., 14 March 1988, personal communication; Oberlander, J.,
24 February 1988, personal communication). The material that was removed
from the secondary clarifier area was disposed of at the Thurston County
Landfill on Margaret Road (Oblas, V., 29 February 1988, personal communi-
cation). According to Mr. R. Alan (14 March 1988, personal communication),
landfill materials remain on the LOTT WWTP site in the area northeast of the
secondary clarifiers.
Commercial and Recreational Marinas—The following five marinas
currently operate in Budd Inlet: West Bay Marina, Olympia Yacht Club,
Fiddlehead Marina, East Bay Marina, and Boston Harbor Marina (see Figure 5).
Although boat painting is allowed at all but the East Bay Marina, boat
repair facilities are only offered at the West Bay Marina. Historically,
the One Tree Island Marina existed near the Fiddlehead Marina. Sediments
contaminated with metals were identified in this area in 1985. As mentioned
below, a plating facility was once located in this area.
Nonpoint sources of microbial contamination in Budd Inlet include
contributions from live-aboards in these Olympia marinas and general boating
45
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activity. These contributions have not been qualitatively or quantitatively
identified.
In addition to these marinas, a U.S. Maritime Fleet ("Mothball Fleet")
was moored in eastern Budd Inlet near Gull Harbor (Jamison, D., 21 January
1988, personal communication; Newall, G., 10 February 1988, personal
communication). This Mothball Fleet may have comprised over 100 boats
including merchant ships, tankers, freighters, and troop transports (Newall,
G., 10 February 1988, personal communication). Scrap material, which may
have included waste oils, solvents, and paints, was reportedly discarded
from the ships into Budd Inlet (Oberlander, J., 29 January 1988, personal
communication). Additional information is not available.
Other Nonpoint Sources—Historical industrial practices may have
contributed contaminants to Budd Inlet. At one time, the Hardel Mutual
Plywood facility located on West Bay Drive (see Figure 5) discharged process
wastes into their onsite septic system (URS 1980). These process wastes
included caustic substances, oil, and phenolic glue wastes (URS 1980). Over
time, these wastes may have leached into Budd Inlet (Oberlander, J., 29
January 1988, personal communication). Also, a plating facility was once
located in the area near One Tree Island Marina [see Figure 5; U.S. Army COE
no date (d)]. This operation may have contributed to the high concen-
trations of cadmium detected in West Bay (Pierce, R., 20 January 1988,
personal communication).
Groundwater
The impact of toxic contaminants from groundwater flow into the study
area is difficult to determine. To date, no studies have defined regional
groundwater conditions in the immediate area of Budd Inlet. The shallow
water table aquifers are most important when evaluating groundwater problems
because of their vulnerability to contamination from surface activities.
The LOTT Urban Area Wastewater Management Plan (Parametrix 1987b) has
addressed groundwater movement and quality in Thurston County, including
identification of sensitive aquifer areas. Much of the area is characterized
46
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by porous soils that allow rapid infiltration of water from onsite disposal
systems into groundwater. According to this plan:
"Approximately 65 percent of Thurston County is underlain by
relatively permeable glacial deposits which overlay unprotected or
shallow aquifers. Nearly 100 percent of domestic water supplies
are derived from these sources. Due to the generally permeable
nature of soils in the County and the location of these aquifers
the entire [study area] is effectively an aquifer recharge area.
Approximately 80,000 people currently dispose of domestic waste
through on-site disposal systems into the study area's aquifer
recharge area. . .. Recent groundwater contamination occurrences
and lake quality degradation that is occurring in the Hicks and
Long Lakes area suggest that the regional assimilation capacity
for on-site disposal systems may be approaching its limit in
selected areas. . .. Due to the sensitivity of County aquifers to
groundwater contamination, the State Department of Ecology has
adopted a State regulation reserving approximately 41,000 gpm of
the area's groundwater resources for future public water supply
needs."
Because the region's groundwater aquifers are recharged primarily from
within the LOTT study area, the continued use of onsite waste disposal
systems for existing uses and new developments without mitigation threatens
the public health in the urban area (Parametrix 1987b).
Groundwater Contamination--
Substantial creosote and PCP contamination of groundwater at the
Cascade Pole Company facility was first documented in 1983 (Norton, D., 5
February 1986, personal communication). A subsequent investigation by
Ecology in February 1985 confirmed the presence of creosote and in ground-
water onsite. Ecology determined that contamination extended to marine
discharges and intertidal sediments in the vicinity of the facility (Johnson,
A., 22 July 1985, personal communication). A subsequent remedial investi-
gation by Applied Geotechnology (1986a,b) provided detailed information on
PAH and phenols in soils and groundwater near the site. High concentrations
of PAH and phenols were present in surface soils in the immediate vicinity
of the pole-treating plant (up to 40,000 mg/kg PAH and up to 400 mg/kg
phenols). Preservative fluid was found floating on the water table in three
wells immediately adjacent to the plant. Concentrations of PAH and phenols
were highest in subsurface soils within a few feet above or below the water
47
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table at sites in the southwestern portion of the property and along the
southern shoreline of the plant. Concentrations of PAH and phenols in
groundwater were highest near the plant and in the southwestern portion of
the property. Using three different methods, Applied Geotechnology (1986a)
calculated the flux (i.e., transport) of PAH and phenols from the fill
aquifer to Budd Inlet. The flux of PAH and phenols to Budd Inlet from
groundwater and surface runoff was estimated to range between 143 and 190
Ib/yr (Applied Geotechnology 1986a). POP accounted for 12 percent (or 17-23
Ib/yr) of the total flux of PAH and phenols to Budd Inlet, and about 23
percent of the total flux of phenols to Budd Inlet.
The only shallow groundwater seep discharges into Budd Inlet that have
been characterized were sampled during investigations conducted at the
Cascade Pole site. On 13 February 1985, Ecology collected water samples
from a shoreline seep located off the Cascade Pole site (Johnson, A., 22
July 1985, personal communication; Norton, D., 5 February 1986, personal
communication). Concentrations of PAH and PCP in the shoreline seep sample
were 2.3 ug/L and 8.6 ug/L, respectively.
In July 1985, Applied Geotechnology (1986a) collected surface water
samples from a seep that discharged beneath the riprap on the eastern
shoreline of the Cascade Pole site. Samples were analyzed for PAH and
phenols. PAH and phenols were undetected in the seep samples. On 24 June
1987, Ecology observed "numerous product seeps" along the shoreline adjacent
to the Cascade Pole site (White, M., 30 July 1987, personal communication).
The product seeps were primarily observed east of Cascade Pole's NPDES-
permitted discharge outfall and approximately 100 ft west of the East Bay
Marina dock. Groundwater seeps were also observed in that area. Ecology
collected a sample from a product seep (Sample CP1) and from an adjacent
groundwater seep (Sample CP2), which were located approximately 100-150 ft
northwest of the East Bay Marina dock. A water sample was also collected
from a groundwater seep (Sample CP3) located approximately 25 ft southeast
of Cascade Pole's NPDES-permitted discharge outfall. Samples were also
collected from a product seep (Sample CP4) and from an adjacent groundwater
seep (Sample CP5), both located approximately 50 ft northeast of the
outfall and 40 ft offshore from the riprap. Samples were analyzed for the
48
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acid/base/neutral extractable organic compounds and volatile organic
compounds on the U.S. EPA priority pollutant list. Sample CP4 was also
analyzed for tentatively identified organic compounds. Analytical results
for these samples are presented in Table 5. Groundwater seep samples
collected southeast of the outfall and from near the East Bay Marina dock
did not appear to be contaminated. In the groundwater seep sample (Sample
CP5) collected northeast of the outfall, concentrations of volatile organics
compounds ranged from 30 to 270 ug/L. Concentrations of organic compounds
ranged from 1,200 to 430,00 ug/L in the product seep sample that was
collected adjacent to the groundwater seep sample. In the second product
seep sample (Sample CP1), elevated concentrations of volatile organic
compounds and PAH were detected. These PAH are typical components of
creosote.
During this investigation, Ecology also surveyed groundwater monitoring
wells for product. Floating product in the wells was estimated by measuring
the distance between the air-oil interface and the oil-water interface.
Floating product was undetected in two wells and detected at <0.01 ft in
three wells. The thickness of floating product in the remaining three
wells, which are located 50 ft south of the Cascade Pole building, ranged
from 4.11 to 7.49 ft. Well N24B was probed for sinking product and none was
encountered.
On 9 March 1988, Ecology detected 1.5 ft of sinking product in
groundwater well SP1 located on the Cascade Pole Company site (Peeler, M.(
15 March 1988, personal communication). The well was installed by Applied
Geotechnology in mid-July 1987 but was never developed or sampled. Ecology
collected samples of the sinking product and surface sheen at this well and
submitted the samples for analysis. Ecology also collected seep samples
onsite on 8 March 1988. Based on these results and negotiations between
Ecology and the Cascade Pole Company, an extensive groundwater sampling
effort may be conducted in the near future.
Although groundwater contamination beneath other industrial areas is
also likely, it has not been investigated. The only past petroleum storage
facilities on Port of Olympia property were operated by Olympia Oil and Wood
49
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TABLE 5. CONCENTRATIONS (ug/L) OF VOLATILE AND EXTRACTABLE ORGANIC COMPOUNDS
IN PRODUCT AND 6ROUNDWATER SEEP SAMPLES COLLECTED IN JUNE 1987 FROM CASCADE POLE COMPANY3
Product
Volatile Qrqanics0
Acetone
Benzene
Toluene
Ethyl benzene
Styrenes
Total xylenes
Aqueous
CP1
U
U
35
190
390E
130E
780E
Fraction
CP1L
430E
U
40
230
540E
190E
l.OOOE
Oil Fraction
CP1
U
U
1.500M
32,000
131,000
42,000
236,000
CP2
U
U
U
U
U
Groundwater
CP3
U
U
2.1
U
0.7M
CP5
30
100
130
U
270
Extractable Orqanics
CP1
CP4
Groundwater
CP2
CP3
Naphthalene
2-methyl naphthal ene
Acenaphthylene
Acenaphthene
Di benzof uran
Fl uorene
Phenanthrene
Anthracene
Fluoranthene
Pyrene
Benzof a) anthracene
Chrysene
Benzo(b)fluoranthene
8enzo(k)fluoranthene
Benzo(a)pyrene
Indeno(l ,2,3-cd)pyrene
Benzo (g,h,i ) pyrelene
Tentatively Identified
1-Methyl naphthal ene
2-Ethanyl naphthal ene
2-Methyl anthracene
Benzoa ( b ) thi ophene
Dibenzothiophene
1-H Indene
2,3,-Dihydro-lH indene
Carbazol e
Tri methyl naphthal ene
2.06E
860,000
18,000
720,000
340,000
410,000
1.3E6
150,000
690,000
420,000
120,000
110,000
82,000
82,000
42,000
12.000J
12.000J
Orqanicsc'd
430,000
240,000
U
130,000
58,000
80,000
220,000
37,000
82,000
98,000
16,000
18,000
10,000
10,000
5.300J
1.200J
1,4000
CP4
490.000J
170.000J
46.000J
40, 000 J
180.000J
100.000J
67.000J
45.500J
360.000J
U
1J
U
5J
2J
3J
9J
U
9J
5J
U
U
U
U
U
U
U
11J
U
U
6J
U
0.7J
U
U
U
U
U
U
U
U
U
U
U
a Only chemicals with detected concentrations are included in this table.
Duplicate sample.
c Data Qualifiers: E=estimated value; J=estimated value is less than the specified detection limit;
M=estimated value of analyte found and confirmed by analyst but with low spectral match parameters; U=compound
was analyzed, but not detected.
d Tentatively identified organic compounds for Samples CP1, CP2, and CP3 are not listed because concentrations
were estimated at <19 ug/L.
Reference: Adapted from M. White (30 July 1987, personal conmunication).
50
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Company and Texaco (Applied Geotechnology 1986a). Applied Geotechnology
(1986a) provided the following information:
"The Olympia Oil and Wood company, opened in 1931, was located
just west of the Georgia Pacific mill [on the southwestern portion
of the peninsula], Olympia Oil and Wood had a 250,000 gallon tank
for No. 6 oil, two 125,000 gallon tanks for No. 5 oil, and two
tanks of unknown capacity to store diesel fuel. Sludge reportedly
was cleaned from the tanks every two to three years, containerized,
and shipped to an oil reclaimer. The bulk storage facility, which
handled approximately 10 to 15 million gallons of oil per year,
was dismantled between 1972 and 1973.
Texaco operated a bulk fuel storage facility west of CPC [Cascade
Pole Company] from 1945 to 1965. The facility had one 105,000
gallon, one 420,000 gallon, and four 630,000 gallon storage tanks
used for kerosene and two grades of gasoline. Annual volume
through the facility was estimated at 25 to 30 million gallons."
In the 1970s, a groundwater investigation was conducted of petroleum
seeps that were observed in an area that was occupied by Standard Oil
(Pierce, R., 20 January 1988, personal communication; Oberlander, J., 29
January 1988, personal communication). The petroleum storage tanks onsite
were removed (Oberlander, J., 29 January 1988, personal communication).
Additional information on this study was not available.
During LOTT's construction of the Water Street Pump Station (see Figure
6), gasoline-contaminated sediments were observed (Ecology 1984; Oberlander,
J., 29 January 1988, personal communication). Groundwater was found to be
"heavily contaminated" by petroleum, and over 83 barrels of contaminated
groundwater were removed from the excavation site between December 1977 and
May 1978 (Ecology 1984). A bulk petroleum storage facility was reportedly
operated in this area by the Mobil Company. However, attempts to finger
print the oil were inconclusive. Ecology conducted a preliminary assessment
at this site and determined that no action was necessary (Ecology 1984;
Spencer, M., 1 February 1988, personal communication). Surface water
contamination has not been observed near the pump station, but is highly
probable given the proximity (<200 ft) of the contaminated groundwater to
Budd Inlet (Ecology 1984). However, because of the bulkheads that exist
between this site and Budd Inlet waters, the gasoline may not be leaching
into Budd Inlet (Oberlander, J., 29 January 1988, personal communication).
51
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Oil-contaminated soils were also observed during the development of the
farmer's market area of Olympia (Pierce, R., 20 January 1988, personal
communication). This contamination was reportedly attributable to bulk
petroleum storage and transfer facilities that had operated in the area.
During demolition of an old gasoline station at the intersection of
East Bay Drive and State Avenue, oil-contaminated soils were also identified.
The gasoline station was reportedly constructed in 1956, and prior to this
date the site was occupied by a grocery store that also had underground fuel
storage facilities. Earth Consultants (1985) conducted a study for ARCO at
this site and installed six monitoring wells. Groundwater was present at a
depth of 9 ft below the surface, and no hydrocarbon accumulations were
noted on the surface of the groundwater. Groundwater samples were collected
and analyzed using gas chromatography. All concentrations of hydrocarbons
were below the 25 ppm detection limit. This value is much higher than the
generally accepted maximum detection limits (e.g., 0.001-5 mg/L). Hydro-
carbon levels in soils were also measured using infrared (IR) spectro-
photometry and silica gel separation. Results indicated that the existing
and previous underground tanks or distribution systems had leaked. In soils
collected from backhoe trenches, Earth Consultants (7 August 1986, personal
communication) reported that "2,500 ppm diesel and 3,400 ppm motor oil were
detected." Gasoline was not detected. In July 1986, Earth Consultants
conducted additional analyses for PCBs and metals using EP toxicity
procedures. Metals were undetected, and PCBs were detected at 0.03 mg/kg.
This concentration is below the 1 mg/kg regulatory action threshold, which
was set as an acceptable cleanup criteria by Ecology (Bradley, D., 30 March
1988, personal communication). The materials removed from this site were
ultimately disposed at the Thurston County landfill, and no contaminated
soils remain onsite (Pierce, R., 20 January 1988, personal communication).
The Thurston County Health Department is currently involved in a 3-yr
groundwater management study (Pierce, R., 17 November 1987, personal
communication). Existing groundwater data are being collected, including
information on aquifers and recharge areas. This groundwater plan will be
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prepared to assess management alternatives for protecting aquifers and will
be available in the near future.
Accidental Spills
Information on accidental spills in the region is contained in files of
complaints reported to Ecology by private citizens. The spills and com-
plaints reported to Ecology since 1986 have been entered into a database.
That database lists the following information: investigator, date of
investigation, alleged violator, material spilled, media code (e.g., surface
water), waterway (e.g., Budd Inlet), and comments. In most cases, the
alleged violator is unknown and there is not enough detailed information to
determine the exact location of the spill or to calculate contaminant
loading.
The 22 reports listed in the database (Ecology, 9 December 1987,
personal communication) are summarized below:
• Nine oil sheens were observed on waterway or beaches
• Five algal blooms were observed
• Fifty gallons of oil were spilled into Budd Inlet via a storm
drain
• "Strip and wax" materials and emulsifiers were dumped into
storm drains that entered Budd Inlet
• Bark and wood wastes from Dunlap Towing, cattle feed waste,
and paint scrapings were discharged to Budd Inlet
• Two unidentified spills were reported.
The only fully documented petroleum spill in Budd Inlet occurred in
1987. Industrial Petroleum Distributors (IPD), Inc. stored process waste
oil at an abandoned ARCO bulk petroleum storage facility on West Bay Drive
53
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(Anderson, D.( 29 October 1987, personal communication; Cloud, G., 30 October
1987, personal communication). Waste oil was spilled onsite, and an
unspecified volume of oil entered Budd Inlet. The oil slick spread at least
as far as Olympia Shoals, and at-sea recovery was attempted. (Cloud, G., 30
October 1987, personal communication). Ecology brought an enforcement
action against IDP. Waste oils were tested for PCBs, and none were detected
(Cloud, G., 30 October 1987, personal communication). Results of a bioassay
on the "remaining contaminated soils" at the IDP site indicated that the
soils were not toxic, and thus they were not designated hazardous wastes
(Anderson, D., 22 December 1986, personal communication). However, onsite
cleanup of oil-contaminated soils may have been conducted by AIRO Services
(Cloud, G., 30 October 1987, personal communication).
EUTROPHICATION
Eutrophic conditions in Budd Inlet have been documented since the 1950s
when Col lias et al. (1962) reported oxygen values below 2.0 mg/L on 4
September 1957 off the Port of Olympia peninsula. Since then, dense
phytoplankton blooms and low dissolved oxygen have been chronic problems in
the southern half of the inlet. Low dissolved oxygen concentrations in the
water column may stress fishes and benthic organisms, and may regulate
benthic infauna communities in the sediments. Therefore, oxygen depletion
may be equally important as toxic contamination for the health of biological
resources.
A total of six data sets were accepted for the review of water quality
in Budd Inlet. The following reports contain data generated since January
1982: Mr. W. Kendra and Mr. T. Determan (6 November 1985, personal communi-
cation), URS (1986), Mr. R. Alan (24 September 1987, personal communi-
cation), Mr. E. Egge (25 January 1987, personal communication), Mr. T.
Mumford (25 September 1987, personal communication), and the U.S. EPA STORET
data files for Ecology ambient monitoring data, 1982-1986 (U.S. EPA, 7
January 1988, personal communication). Data contained in these documents
have been used to determine annual fluctuations, sources, and budgets of
nutrients and dissolved oxygen, in addition to the effects of WWTP discharges
54
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on marine receiving water quality. These data were collected at the water
quality stations shown in Figure 7.
Relationship Between Nutrients and Dissolved Oxygen Depletion
Oxygen depletion typically occurs in the near-bottom water (0-2 m above
the sediment surface) when flushing is inadequate to renew bottom water, and
vertical mixing is reduced or eliminated due to a density-stratified water
column (Yake, B., 6 July 1981, personal communication; Welsh, B.( 18 November
1987, personal communication). These conditions frequently exist in
shallow estuaries with an established thermocline during the late summer.
Oxygen depletion is enhanced by the addition of organic materials because
they provide the necessary nutrients for algal growth. Dense algal blooms
often result under such conditions. Algal production of oxygen in the near-
surface water may supersaturate it, but as these organisms die and sink to
the sediment, their subsequent decomposition [in addition to regular
sediment oxygen demand (SOD)] depletes available oxygen in the bottom water.
A vertical profile of dissolved oxygen in a water column experiencing
similar conditions might show oxygen concentrations ranging from 12 to over
15 mg/L near the water surface and concentrations of less than 3.0 mg/L near
the bottom. A typical vertical profile showing oxygen depletion in an area
similar to Budd Inlet is depicted in Figure 8. The most rapid decreases in
oxygen concentration with depth usually occur in the photic layer. Under
conditions of poor flushing, a rapid decline in dissolved oxygen caused by
SOD may also occur approximately 0-2 m above the sediment. In the absence
of vertical mixing or flushing, these conditions would persist until the
algal bloom became nutrient limited and growth subsided.
Dinoflagellates, specifically Cerative fusus. and Noctiluca scitallaus
(in 1977; Kruger 1979), and Gvmorodinium spp. and Ceratium spp. (in 1984;
URS 1986), dominate the severe late summer algal blooms. Because dinoflag-
ellates may migrate diurnally, they may be net producers of oxygen in the
surface waters during the day, and consumers of oxygen in the bottom waters
at night. URS (1986) suggested that vertical migration of dinoflagellates
was a major contributor to oxygen depletion of near-bottom water in Budd
55
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SAMPLING STATIONS
A WATER QUALITY
A WATER QUALITY - LOTT
A WATER QUALITY - URS (19B6)
• FECAL COLIFORM BACTERIA
OLYMPIA
CITY
| BOUNDARY
Figure 7. Locations of water quality and fecal coliform bacteria
sampling stations in Budd Inlet.
-------
DISSOLVED OXYGEN (mg/L)
0 2.0 4.0 6.0 8.0 10.0 12.0 14.0
I I I I I I I I I I L I I I I
1.0 -
2.0 -
3.0 -
4.0 -
5.0 -
Q.
UJ 6.0 H
Q
7.0 -
8.0 -
9.0 -
10.0 -
11.0 -"*;..:•:::,•.-.;.•:,:
SUBSURFACE
MAXIMUM
SEDIMENT
OXYGEN
DEMAND
Figure 8. Theoretical example of vertical profile of dissolved oxygen.
57
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Inlet during the late summer. Further field studies are required to
substantiate this theory.
Nutrients
Nutrients enter the Budd Inlet water column through tidal exchange and
flushing from Puget Sound, benthic flux, and nutrient loading from point and
nonpoint sources within the inlet. Each of these sources contributes a
substantial amount of nutrients, and collectively they provide enough
nutrients to sustain dense phytoplankton blooms. URS (1986) determined that
the limiting nutrient for algal growth in Budd Inlet is nitrogen. Typically,
nitrogen is the limiting nutrient in marine systems, whereas phosphate is
the limiting nutrient in freshwater systems. Nitrogen and phosphate
concentrations in Budd Inlet fluctuate during the year in response to
changes in the nutrient concentration of Puget Sound, uptake by phytoplank-
ton, and source loadings.
Water quality data were collected from December 1981 to October 1982
near the Washington Department of Natural Resources (WDNR) Marine Station,
located south of Gull Harbor (Mumford, T., 25 September 1987, personal
communication). This sampling site is adjacent to the Seashore Villa WWTP
discharge, and may be affected by the discharge of sewage effluent. These
are the only Budd Inlet nutrient data collected for a complete year. The
Ecology ambient monitoring program currently requires the collection of
surface and bottom water quality data at two Budd Inlet stations [i.e.,
Station BUD002 north of Fiddlehead Marina in West Bay and Station BUD005
south of Olympia Shoals (U.S. EPA, 7 January 1988, personal communication)].
Water quality at Station BUD002 is influenced by the LOTT 48-in diameter
outfall at the Fiddlehead Marina, the LOTT 30-in diameter primary outfall,
and the Capitol Lake outfall. Analytical results of samples collected at
Station BUD005 suggest minimal anthropogenic influences. The water quality
at this station should be similar to that at the WDNR Marine Station.
58
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Nitrogen--
Nitrogen concentration in water is presented as the sum of nitrate and
ammonium. These are the forms of nitrogen that are most readily assimilated
by phytoplankton, and therefore reflect the nitrogen available for algal
growth. The maximum concentration at the WDNR Marine Station was 0.97 mg/L
in early December, while the minimum concentration was 0.01 mg/L at the end
of August (Figure 9) (Mumford, T., 25 September 1987, personal communica-
tion). Nitrogen appeared to have been higher during the spring and fall at
the WDNR Marine Station than at Ecology Station BUD005, possibly in response
to the Seashore Villa WWTP effluent discharge. Ecology examined water
quality in relation to this discharge and found that some nutrient levels
inshore of the discharge were slightly elevated (Kendra, W. and T. Determan,
6 November 1985, personal communication).
Normal seasonal variability between 1982 and 1986 is most easily
reflected in the monthly mean nitrogen concentrations at Station BUD005.
Maximum nitrogen concentrations decreased from 0.18 mg/L between April and
July to 0.09 mg/L between July and mid-September. In September, the water
column generally becomes mixed due to strong winds and the influx of Puget
Sound water, which contains higher nutrient concentrations. Nitrogen levels
increased at Station BUD005 and were more variable (range 0.01-0.12 mg/L)
during the fall.
Average nitrogen values in both the surface water and bottom water were
lower at Station BUD005 than at Station BUD002. Nutrient concentrations may
be elevated at Station BUD002 because of its proximity to the LOTT outfall at
the Fiddlehead Marina and to the Capitol Lake outfall (Figure 10). Effluent
released from the LOTT WWTP at Station BUD002 results in higher concentra-
tions of nitrogen at Station BUD002 and greater variability than at Station
BUD005. The lowest nitrogen concentrations that occurred between 1982 and
1986 were during summer.
Source surveys and dynamic modeling were conducted by URS (1986) to
identify the relative contributions of specific sources to the Budd Inlet
59
-------
WDNR MARINE STATION
i
D>
on
o>
Q.
0.9 -
0.8 -
0.7 -
0.6 -
0.5 -
0.4 -
0.3 -
0.2 -
0.1 -
JAN FEE MAR APR MAY JUN JUL AUO SEPT OCT NOV DEC
1982 1981
0.3
0.28 -
0.26 -
0.24 -
0.22 -
0.2 -
0.18 -
0.18 -
0.14 -
0.12 -
0.1 -
0.08 -
0.06 -
0.04 -
0.02 -
JAN FEB MAR APR MAY JUN JUL AUG SEPT OCT NOV DEC
1982 1981
MONTH
Reference: Data from Mumford, T. (25 September 1987, personal communication).
Figure 9. Annual variation in nitrogen and phosphate in surface
waters at the WDNR Marine Station, 1981-1982.
60
-------
O>
Z
Z
o"
0.35 -
0.25 -
0.2 -
0.15 -
o.i -
0.05 -
BUD002
MAR APR MAY MN JUL AUG SEPT OCT NOV DEC
0.35 -
O> 0.3 -
v>
X
0.25 -
0.2 -
0.15 -
0.1 -
0.05 -
BUD005
D SURFACE
NITROGEN
+ BOTTOM
NITROGEN
MONTHLY AVERAGE,
SURFACE
MONTHLY AVERAGE,
BOTTOM
a a
DD
MAR APR MAY JUN
JUL AUG SEPT OCT NOV DEC
MONTH
Reference: Data are provided in Appendix B.
Figure 10. Temporal variation in nitrogen [sum of nitrate (NO3)
and ammonium (NHg)] at Ecology ambient water quality
monitoring stations BUD002 and BUD005, 1982-1986.
61
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nutrient budget. A two-dimensional box model for Budd Inlet included point
sources, flushing rates, and benthic release. Puget Sound water was found
to supply approximately 60 percent of all the nitrogenous nutrients to the
inlet. Both the LOTT WWTP and bottom sediments (i.e., benthic release)
supplied about 20 percent of nitrogen each. A survey of point sources
provided a relative breakdown of inputs. Nearly 100 percent of the nitrite,
and the majority of the nitrate, originated from the LOTT WWTP (URS 1986).
The relative contribution of major sources of nitrogen to Budd Inlet and to
the upper 3 m of the water column is shown in Table 6. Elevated concentra-
tions of nitrogen at Station BUD002 (compared with Station BUD005) result
from nitrogenous compounds discharged from the LOTT WWTP through both the
LOTT outfall and the Fiddlehead Marina outfall. The relative contribution
of specific sources exclusively to southern Budd Inlet were not determined.
Phosphate--
Phosphate is reported as orthophosphate (PO/j-P), the form most readily
assimilated by phytoplankton. This nutrient is not generally limiting to
marine phytoplankton growth at any time of the year. Phosphate data from
the WDNR Marine Station indicate that concentrations were generally below 0.1
mg/L (Mumford, T., 25 September 1987, personal communication), and seasonal
depletion was not evident in Budd Inlet (see Figure 9).
The primary difference between phosphate concentrations at Station
BUD005 and at Station BUD002 is that Station BUD002 occasionally exhibits
very high concentrations of phosphate (Figure 11). It is doubtful that
these concentrations are the result of natural fluctuations. The fluctu-
ations probably result from nutrient inputs by the LOTT WWTP. The Budd
Inlet source study conducted by URS (1986) revealed that the LOTT WWTP
contributed over 90 percent of the phosphate from known point sources.
The temporal variability in nitrogen and phosphorus concentrations at
Station BUD002 from 1982 to 1986 were remarkably similar, most likely in
response to nutrient loadings from the LOTT WWTP- In most cases, very high
nitrogen values corresponded to very high phosphate values. For example,
samples collected on 23 September 1985 contained the highest recorded
62
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TABLE 6. RELATIVE CONTRIBUTION OF SOURCES OF NITROGEN TO BUDD INLET
Nitrate and Ammonium
Source Nitrite (Percent) (Percent)
A) Upper 3 m of water column
Puget Sound 78 20
LOTT WWTP 22 80
Bottom sediments (i.e.,
benthic release)
B) Entire Water Column
Puget Sound 92 20
LOTT 8 36
Bottom sediments (i.e., -- 44
benthic release)
Reference: URS (1986).
63
-------
0 "0
0.26 -
0.24 -
0.22 -
^-J» 0.2 -
~
O) 0.18 -
E
•C- 0.16 -
n
i 0.14 -i
O 0.12 -
Q.
0.1 -
0.08 -
0 06 -
0.04 -
A no — .
BUD002 D
D
•f
+
* ^
+ D / V
.A. n t -a? 0
+ / ID / A^\ /
D / ^\ "*" A" ./^*^\""~'A-. '
A* J1BB — " V^L*>- '' \ /*C
+ *B •*•-""' + DfD * — tf + V C Is*
B + + B B D +
a a D B n +
MAR APR MAY JUN JUL AUG SEPT OCT NOV DEC
n T
u.w
0.28 -
0.26 -
0.24 -
0.22 -
2* 0.2 -
0) 0-18 -
C 0.16 -
Q. 0.14 -
Vr 0.12 -
O
tL 0.1 -
0.08 -
0.06 -
0.04 -
0.02 -
O SURFACE MONTHLY AVERAGE,
PHOSPHATE SURFACE
+ BOTTOM MONTHLY AVERAGE,
PHOSPHATE BOTTOM
+
m
+ a-
a -t- D n o -A^~
•4- ^-^^^^^s.
0j- 5^-* ^t— — "*~~ — ^2^ *^ ^^^>_ * ^
B Afifr^ A't^*"^*^fh^fcg'^ D 45^*^r "^^J* ™W—FA
Q v^ ^** B3 ^^fr^"^^ ~ •(• B B +• B
+ B >K5 B a -t- B
™
0_
T r i i i i i i i i
MAR APR MAY JUN JUL AUG SEPT OCT NOV DEC
MONTH
Reference: Data are provided in Appendix B.
Figure 11. Temporal variation in phosphate at Ecology ambient
water quality monitoring stations BUD002 and BUD005,
1982-1986.
64
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surface and bottom water nitrogen, highest recorded surface water phosphate,
and second highest recorded bottom water phosphate. The bottom water on 25
June 1984 contained the highest recorded phosphate and second highest
nitrogen. Monthly average concentrations of nitrogen and phosphate (see
Figures 10 and 11) followed similar patterns.
Water quality investigations at the three WWTP in central and northern
Budd Inlet also demonstrated the effect of municipal effluents on water
quality. Surveys were conducted at control, mixing zone, and nearshore
sites at Tamoshan WWTP and Seashore Villa WWTP, and at control and mixing
zone sites at Beverly Beach WWTP (Kendra, W. and T. Determan, 6 November
1985, personal communication). Nutrient concentrations in the mixing zone
at the Tamoshan WWTP were less than at the upcurrent control, but in all
other cases, nutrient concentrations were greater than at control sites.
Beverly Beach WWTP exhibited the highest nitrate, orthophosphate, and total
phosphate concentrations, while Tamoshan WWTP exhibited the highest ammonium
concentrations.
Dissolved Oxygen
Dissolved oxygen is a sensitive indicator of the health of a water body
because it is the result of complex interactions among physical and biolog-
ical variables. Oxygen levels vary naturally as a result of seasonal
changes in solar radiation, wind, vertical mixing, flushing, nutrient
levels, algal blooms, and sediment oxygen demand. When oxygen concentrations
are less than 3 mg/L (termed hypoxia), organisms become stressed due to the
lack of oxygen (Rhoads, D., 18 November 1987, personal communication).
Mobile species often move away from hypoxic areas while seeking more
oxygenated water (Welsh, B.. 18 November 1987, personal communication).
Tolerant sedentary species will survive provided that the duration of the
hypoxic event is short and the oxygen concentrations generally remain above
1.0 mg/L. Anoxia, defined as 0.1 mg/L oxygen or less, results in widespread
mortality of vertebrates and invertebrates in the affected area (Welsh, B.,
18 November 1987, personal communication).
65
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Budd Inlet experiences large fluctuations in oxygen concentration that
result from the complex interactions between physical, biological, and
anthropogenic variables (e.g., nutrient loadings from municipal effluents;
URS 1986). It is not unusual for dissolved oxygen concentrations in the
southern portion of the inlet in late summer and early fall to be below the
Washington Station Class B water quality standard 5.0 mg/L. During this
time of the year the water column is frequently well stratified due to
lengthy periods of calm sunny days that increase the near-surface water
temperature and, in conjunction with high nutrient loadings from the LOTT
WWTP, provide suitable conditions for dense algal blooms (URS 1986).
Flushing is reduced during this time of year and Puget Sound water contains
less oxygen. Also, the discharge of ammonia from the WWTP combined with
warmer water temperatures increase the rate of nitrification resulting in
more localized oxygen depletion near the WWTP outfalls.
A total of five data sets, including the Ecology ambient monitoring
data, were available for the review of dissolved oxygen data in Budd Inlet
from 1982 to 1987 (see Appendix A, Table A-5). These reports, in addition
to a number of older publications, indicate that oxygen depletion has been a
severe problem in Budd Inlet for several decades. Although the magnitude
and geographic extent of oxygen depletion vary annually, the most severe
depletion usually occurs south of Priest Point. For example, in August 1977
the oxygen concentrations were below the 5.0 mg/L Class B water quality
standard from Olympia to nearly Tykle Cove, with the lowest values of less
than 1.0 mg/L in East and West Bays (Figure 12) (U.S. Army COE 1977).
Variability in Dissolved Oxygen--
Dissolved oxygen is routinely monitored 1) by the LOTT WWTP at five
locations (Stations 1-5) (Alan, R., 24 September 1987, personal communica-
tion), 2) by the Port of Olympia in the East Bay Marina (Egge, E., 1
February 1988, personal communication), and 3) by Ecology at Stations BUD002
and BUD005 (U.S. EPA, 7 January 1988, personal communication) (see Figure
7). The only data that were collected over an entire year are the LOTT WWTP
data in 1986 (Figure 13). The distribution of dissolved oxygen at the five
stations was remarkably similar, although the absolute concentrations often
66
-------
A
6.85
• 4.40
BUDD
INLET
\\
r..
2000
500
4000
feet
meters
1000
U.S. ARMY COE
ECOLOGY
ROUTINE MONITORING
\
Reference: Adapted from U.S. Army COE (1977).
Figure 12. Distribution of dissolved oxygen in the bottom waters
of upper Budd Inlet, 17-18 August 1977.
67
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FIDDLEHEAD MARINA
OCT MOV DEC
O)
E
LU
o
>
X
o
D
LU
o
(/)
C/5
5
SEPT OCT NOV DEC
- LOTT OUTFALL (30 in)
JAN FtB M*fl APR MAY JUN JUL AUG SEPT OCT NOV DEC
MID-CHANNEL
FCB UAf) APR tUY MH JUL AJJO SEPT OCT NOV OCC
SURFACE DO
BOTTOM DO
CAPITOL LAKE OUTFALL
CLASS B WATER
QUALITY STANDARD
HYPOXIA
FEB UAA APf) UAY JUN JUL AUO SCPT OCT NOV OCC
MONTH
Reference: Data from Alan, R. (24 September 1987, personal communication).
Figure 13. Monthly variation in dissolved oxygen (DO) measured
at the five LOTT WWTP monitoring stations in 1986.
68
-------
differed. Oxygen depletion was most severe at the Capitol Lake outfall
where oxygen levels 2.0 ft above the sediment were less than 4.0 mg/L.
Near-bottom oxygen levels below the 5.0 mg/L Class B water quality standard
occurred consistently at the other stations.
Dissolved oxygen data collected between 1982 and 1986 at Stations
BUD002 and BUD005 followed a similar pattern, although levels at Station
BUD005 were generally higher than at Station BUD002 (Figure 14). Mean oxygen
levels in the surface water were usually 1.0-3.0 mg/L higher than mean
bottom water concentrations. In late summer, the mean bottom water concen-
tration over the 5-yr period was less than the 5.0 mg/L Class B dissolved
oxygen standard. On two occasions, values below 3.0 mg/L were observed.
The remaining dissolved oxygen data were collected by the Port of
Olympia at the East Bay Marina (Egge, E., 25 January 1987, personal communi-
cation). These data were collected using a Leeds and Northrup model 7931
dissolved oxygen probe or by Winkler titrations of water samples. Values
generated with the Leeds and Northrup probe frequently varied by 30-50
percent from the Winkler values despite the probe's stated accuracy of + 1
percent. Because data generated with Winkler titrations are considered more
reliable than data generate with probes, only these data were reviewed for
this report.
The East Bay Marina maintains an aeration system with 18 aerators
located throughout the marina docks (Egge, E., 1 February 1988, personal
communication). Operation of this system is supposed to be based on
dissolved oxygen fluctuations. When dissolved oxygen is less than 6 mg/L
for over 6 h (consecutive), the aerators are turned on. They remain on
until dissolved oxygen levels exceed 6 mg/L. Because the oxygen probe was
not reliable, other criteria such as wind and length of sunny periods are
often used in conjunction with oxygen concentration to determine operation
of the aerators (Arden, H., 11 February 1988, personal communication).
Diver observations confirmed that use of the aeration system does not cause
sediment resuspension (Arden, H., 10 February 1988, personal communication).
Dissolved oxygen measurements are taken at two locations in the East Bay
Marina: at the end of the transient moorage dock (Dock A; minimum depth 4 m)
69
-------
O)
Q
UJ
>
_J
O
CO
CO
o
14
-*
CLASS B WATER
QUALITY
STANDARD
HYPOXIA
MAR APR MAY JUN JUL AUG SEPT OCT NOV DEC
D SURFACE DO ---
+ BOTTOM DO
MONTHLY AVERAGE,
SURFACE
MONTHLY AVERAGE,
BOTTOM
CLASS B WATER
QUALITY
STANDARD
HYPOXIA
MAR APR MAY JUN JUL AUG SEPT OCT NOV DEC
MONTH
Reference: Data are provided in Appendix B.
Figure 14. Temporal variation in dissolved oxygen (DO) at
Ecology ambient water quality monitoring stations
BUD002 and BUD005, 1982-1986.
70
-------
and at the base of Dock J (minimum depth 2.7 m). The measurements are taken
almost daily from Monday to Friday. Dissolved oxygen declines throughout the
summer, and the aeration system is unable to prevent dissolved oxygen from
declining below the 5 mg/L Class B water quality standard (Figure 15).
Bottom water dissolved oxygen at Station J is frequently hypoxic in August
and September (i.e., less than 3.0 mg/L).
It was noted by Port of Olympia personnel that the aeration system is
used less when oxygen levels are determined with Winkler titrations than when
oxygen is measured with the probe (Egge, E.( 1 February 1988, personal
communication). Winkler titrations are collected near the water surface, in
the middle of the water column, and at the bottom where the probe is
situated. Operation of the aeration system is therefore not always based on
oxygen levels in the bottom water layer, which are usually lowest due to
SOD. Reoxygenation of the bottom water might occur more readily if the data
used to determine use of the aeration system were obtained from the bottom
of the water column rather than the middle or surface of the water column.
Qualitative information on low dissolved oxygen levels was provided by
the Salmon Culture Division of the Department of Fisheries (Peck, L., 18
March 1988, personal communication). During the past 5 yr, the Salmon
Culture Division has been actively involved with trapping adult chinook
salmon at the Fourth Street bridge from mid-August to mid- or late-September.
During this operation, dissolved oxygen levels have been measured at 2.5 mg/L
and below. The most severe levels of dissolved oxygen occurred during high
slack tides, and it was observed that levels could vary dramatically within
any 24-h period.
Dynamics of Dissolved Oxygen in Budd Inlet--
The comprehensive water quality study conducted by URS (1986) in Budd
Inlet was designed to determine the cause of oxygen depletion, and to
identify measures that might alleviate the problem. The following discussion
summarizes some of their findings.
71
-------
EAST BAY MARINA, DOCK J
0)
E
LJ
O
>
X
O
Q
HI
O
en
en
Q
CLASS B WATER QUALITY STANDARD
HYPOXIA
---^ J—rW—r CLASS B WATER QUALITY STANDARD
CLASS B WATER QUALITY STANDARD
HYPOXIA
DATE
SURFACE DO » MIDDLE DO « BOTTOM DO
Figure 15. Daily variation in dissolved oxygen (DO) in the surface,
middle, and bottom waters near the East Bay Marina,
summer 1986.
72
-------
Data were generated from two intensive surveys and from field-verified
steady-state and dynamic models. In September 1984 and May 1985, dissolved
oxygen was measured at eight stations distributed throughout the inlet (see
Figure 7). These data were used to calibrate the models. In September
1984, oxygen levels were extremely high near the water surface (18-20 mg/L)
and low near the bottom (<5 mg/L), indicating a highly stratified water
column. A dense dinoflagellate bloom was observed in the surface waters.
During this intensive survey, a storm moved through the study area and the
accompanying winds disrupted the vertical stratification of the water
column. This storm caused a change in oxygen concentrations in the water
column, and bottom concentration increased from 4 to 5 mg/L while surface
concentration decreased from 20 to 9 mg/L. Oxygen concentrations the
following May 1985 ranged from a near-surface high of approximately 15 mg/L,
to a near-bottom low of about 9 mg/L. An algal bloom composed of diatoms was
observed.
Both a steady-state and a dynamic water quality model were fit to Budd
Inlet to determine the combinations of LOTT WWTP discharge volume, effluent
nutrient removal, and outfall location that would minimize the dissolved
oxygen problem. The biochemical processes that were incorporated into the
dynamic model included SOD, 8005, chlorophyll a., phaeopigments, fecal
pellets, organic nitrogen, ammonium, nitrite, and nitrate. Physical
processes that were incorporated included wind; waterbody geometry; time-
varying boundary condition data; source, sink, and reaction rates for each
of the constituents being simulated; and hydraulic and physical variables.
The dissolved oxygen simulations were limited to use of the May 1985 data
because no quantitative dynamic model of the September 1984 dinoflagellate
bloom exists. However, the effect of nutrient addition on the strength and
duration of the September 1984 dinoflagellate bloom may be greater than the
effect of nutrient addition on the May 1985 diatom bloom. Diatom blooms are
limited by available light, whereas dinoflagellates have the ability to grow
at lower light levels and to migrate to their optimum light level. Because
dinoflagellates also have the ability to take up nutrients during the day
and night, the magnitude of the bloom would likely be nutrient-limited
rather than light-limited. Because of the readily available nutrient supply
from LOTT, dinoflagellate blooms may exist for extended periods of time, and
73
-------
may result in severe oxygen depletion. The duration of these blooms is
probably controlled by meterological and hydrodynamic conditions that
disrupt the vertical stratification of the water column and the vertical
migrations of the dinoflagellates. The reader is directed to URS (1986) for
details of the model and calibration procedures.
Dynamic modeling results showed that the spring diatom bloom is
enhanced at least 30 percent in the inner portions of Budd Inlet by the
existing nutrient loadings from the LOTT WWTP. However, those model results
were not supported by data collected at the WDNR Marine Station, which
indicated that the concentration of nitrogen is not a limiting nutrient in
the spring. The model indicated that aside from elimination of this
discharge, the best option to reduce the diatom blooms is to remove nutrients
from the effluent. Relocation of the LOTT discharge pipe away from the
inner inlet would reduce the strength of the bloom. But, regardless of the
discharge location, the bloom without nutrient removal would be 30-50
percent stronger than the bloom with nutrient removal. Predicted SOD was
directly related to diatom production. It was predicted to be 10-15 percent
greater in the inner inlet without nutrient removal than with nutrient
removal.
Summary and Recommendations--
Water quality conditions in Puget Sound in late summer and early fall
aggravate the oxygen depletion problem. Flushing rates are lower than in
the spring, as are dissolved oxygen concentrations in the water that flushes
Budd Inlet. Water temperature and SOD are higher in late summer and early
fall than in spring. Coupled with blooms of vertically migrating dinoflag-
ellates, oxygen depletion becomes a severe problem at this time of the year.
Recommendations for changes to the LOTT discharge configuration were
developed based on the conclusion that the presence and persistence of
dinoflage!late blooms in late summer and early fall were the probable cause
of the low dissolved oxygen problems. Under state water quality standards,
natural dissolved oxygen levels may be degraded by up to 0.2 mg/L by
anthropogenic activities. The results of these modeling efforts indicate
74
-------
that this standard is frequently exceeded. Under recommendations from
Ecology, URS (1986) concluded that a maximum algal bloom enhancement of 10
percent above the no-discharge scenario would be acceptable, and would
reduce the potential magnitude of oxygen depletion during the late summer
and early fall to acceptable levels. To achieve these levels, URS (1986)
recommended that at the present outfall location, the average wet weather
flow (AWWF) of 16.3 MGD be maintained in addition to removal of at least 90
percent of the nutrients from April through October. For any outfall
location within the inlet, or for a flow increase of up to 22 MGD (AWWF).
URS (1986) recommended at least 90 percent nutrient removal.
MICROBIAL CONTAMINATION
General Overview
Microbial contamination of water and shellfish has long been considered
a public health risk. Swimming in water or consuming shellfish that are
contaminated with enteric bacteria and viruses can result in gastroenteritis,
nausea, diarrhea, typhoid fever, cholera, and hepatitis. Based on past
research, the bacteria of primary concern are enteric pathogens excreted in
human and animal feces, such as Salmonella spp., Yersini enterocolitica.
Campylobacter fetus. Vibrio parahaemolyticus. and Vibrio cholerae (Munger et
al. 1979).
The current Washington State standards for commercial shellfish
harvesting and recreational use are based on the concentration of fecal
coliform bacteria in water and shellfish tissue [Washington Administration
Code (WAC) 173-201-045; Lilja, J., 6 June 1985, personal communication].
The Washington State fecal coliform bacteria standard for waters used for
harvesting shellfish is the same as the standards adopted by the Interstate
Shellfish Sanitation Conference (Lilja, J., 25 March 1988, personal
communication). Because shell fish feed on small particles filtered from
the water, these standards are stricter than the U.S. EPA standards for
primary recreational waters. Some free-living bacteria and viruses that are
attached to particles become concentrated in the gut of filter-feeding
75
-------
bivalves (Colwell and Listen 1960; Kelly et al. 1960; Mitchell et al. 1966).
Because there are no documented cases of human illness resulting from
eating commercially harvested shellfish from the State of Washington, the
standards for allowable concentrations of fecal coliform bacteria in the
water column and shellfish tissue are considered conservative (Lilja, J.( 6
June 1985, personal communication).
Data Synthesis
Choice of Indicators--
Because fecal coliform bacteria have been widely used as a microbial
indicator of water quality, the following analysis is based on available
data for fecal coliform bacteria concentrations in Budd Inlet. Data on
microbial indicators other than fecal coliform bacteria are not available
for the project area. However, U.S. EPA has proposed the use of enterococci
bacteria in place of fecal coliform bacteria because a close correspondence
in the distributions of enterococci bacteria and pathogenic microbes has
been found, and enterococci are associated with human illness (e.g.,
gastroenteritis).
Available Data and Station Locations--
Bacteriological measurements in Budd Inlet have been made primarily in
a comprehensive study of circulation and water quality in Budd Inlet (URS
1986), in the ambient water quality monitoring program conducted by Ecology
(U.S. EPA, 7 January 1988, personal communication), and by the City of
Olympia (Alan, R., 24 September 1987, personal communication). Sampling
stations are depicted in Figure 7. Other data were supplied for Boston
Harbor (R.W. Beck and Associates 1986), WWTP (Kendra, W. and T. Determan, 6
November 1985, personal communication), and the East Bay Marina (Pierce,
R., 22 October 1987, personal communication). Data were also available for
shellfish collected near Priest Point (Armstrong, J., 17 November 1987,
personal communication). Data on microbial contamination from nonpoint
76
-------
sources (e.g., live-aboards in Olympia marinas, general boating activities
in Budd Inlet, hobby farms, failing septic systems) were not available.
Reference Data--
Reference data are based on Washington State standards for fecal
coliform bacteria concentrations in water [Ecology and Washington Department
of Social and Health Services (DSHS)] and in shellfish (DSHS) . Ecology
standards for fecal coliform bacteria for the waters of the project area are
listed below:
• Class A Marine - "...shall not exceed a geometric mean value
of 14 organisms/100 ml with not more than 10 percent of
samples exceeding 43 organisms/100 mL" [WAC 173-201-045(2)-
Class B Marine - "...shall not exceed a geometric mean value
of 100 organisms/100 mL, with not more than 10 percent of
samples exceeding 200 organisms/100 ml" [WAC 173-201-045(3)-
The maximum allowable fecal coliform bacteria levels for commercial shellfish
harvesting areas certified by DSHS are listed below:
• Shellfish tissue - 230 organisms/100 g (U.S. Food and Drug
Administration guidelines)
• Water - A median of 14 organisms/100 mL with not more than 10
percent of the samples exceeding 43 organisms/100 mL (note:
this is virtually identical to the standard for Class A marine
waters; see above) .
77
-------
Elevation Above Reference (EAR) Analysis--
The geometric means for fecal coliform bacteria concentrations were
calculated from all available information. Fecal coliform data from Ecology
Stations BUD002 and BUD005 were averaged over 1982-1986. Data from five
stations sampled by the City of Olympia were averaged over 1986. Approxi-
mately half of the 57 stations surveyed for the URS (1986) report were
sampled once while the remaining stations were sampled twice. The data are
reported as averages when possible. All data from Boston Harbor were
averaged because specific sampling locations were unclear. Data from
individual sites along the shores of Budd Inlet (URS 1986) were grouped by
area to obtain a sufficient sample size for calculation of a geometric mean.
EAR values were calculated by dividing the geometric mean bacterial
concentration by the appropriate standard stipulated in WAC 173-201-045
(Table 7). For example, the geometric mean concentration at Station BUD005
(located near Olympia Shoals in Class A marine waters) was 2 organisms/100
mL and the calculated EAR is 0.14 based on the Class A marine water standard
(see Table 7). In addition, none of the samples exceeded this standard of
a maximum of 43 organisms/100 mL. EAR values were calculated in a similar
manner for the remaining data (Figure 16, Table 7). Note that the water
quality standards differ between Class A and Class B marine waters.
EAR values greater than 1 indicate that the geometric mean concentration
exceeded the standard. EAR values below 1 indicate that the geometric mean
concentration was below the water quality standard. The calculated EAR
values (see Table 7) indicate that water quality standards were not exceeded
at the Ecology Ambient Water Quality Monitoring Program stations (BUD002 and
BUD005), nor were they exceeded off the LOTT WWTP outfalls. Moxlie Creek
was the only site to exceed Class B water quality standards (EAR=21.9).
Class A standards were exceeded near the Tamoshan and Beverly Beach WWTP, in
Boston Harbor, in Ellis Cove, south of the Seashore Villa WWTP, off Athens
Beach, north of Butler Cove, and in Butler Cove. More than 10 percent of
the samples collected between Priest Point and Seashore Villa, in Boston
Harbor, and off the Tamoshan WWTP exceeded standards.
78
-------
TABLE 7. FECAL COLIFORM BACTERIA DATA AND MEAN EAR VALUES
FOR BUDD INLET, 1982-1987a
Fecal Col i form Bacteria/lOOmL
Number of
Number Samples Geo-
of per Minimum Maximum metric
Area Stations Station Value Value Mean EAR
West Bay offshore 1 36 3 70 16
Western shoreline, 6 1 0 25 4
West Bay
Capitol Lake outfall 1 14 2 60 13
Fiddlehead Marina 1 14 1 60 9
Near LOTT 30-in outfall 3 Varied 0 33 6
East Bay Marina 3 Varied 1 23 5
Moxlie Creek 1 2 2,000 2,400 2,190
Eastern shoreline, 5 1 or 2 2 870 59
East Bay
Ellis Cove 2 2 75 1,230 334
Priest Point 1 7 18 7,000 206
Priest Point to 8 1 or 2 0 2,000 34
Seashore Villa
Seashore Villa 7 1-3 0 920 9
Gull Harbor to 6 1 or 2 0 2,400 11
Dofflemeyer Point
Boston Harbor 28 1 or 2 23 2,400 151
Cooper Point to 3 1 0 1,020 10
Tamoshan
Tamoshan 6 1 or 2 0 2,000 28
Beverly Beach 2 1 or 4 0 1,141 19
0.16
0.04
0.13
0.09
0.06
0.05
21. 9d
0.59d
23. 9d
0.90e
2.5
0.7d
0.8d
10. 8e
0.72d
2.04e
1.36d
Marine
Water Use
Classifi-
cation Reference
Class B U.S. EPA
(7 January 1988)c
Class B URS (1986)
Class B Alan
(24 September 1987)°
Class B Alan
(24 September 1987)°
Class B URS (1986),
Alan
(24 September 1987)°
Class B Alan
(24 September 1987 )c,
Pierce
(22 October 1987)c
Class B URS (1986)
Class B URS (1986),
Pierce
(22 October 1987)c
Class A URS (1986)
Shellfish Armstrong
(17 November 1987)e
Class A URS (1986)
Class A URS (1986),
Kendra and Determan
(6 November 1985) c
Class A URS (1986)
Class A URS (1986)
R.W. Beck and
Assoc. (1986)
Class A URS (1986)
Class A URS (1986),
Kendra and Determan
(6 November 1985)°
Class A URS (1986),
Kendra and Determan
(6 November 1985) c
79
-------
TABLE 7. (Continued)
Fecal Coliform Bacteria/lOOmL
Number of
Area
Athens Beach
Tykle Cove
Olyrnpia Shoals
Between Tykle and
Butler Coves
Butler Cove
Number
of
Stations
3 1
2
1
1
3
Samples
per
Station
or 2
1
36
2
2
Minimum
Value
0
0
1
310
0
Maximum
Value
2,400
0
26
370
800
Geo-
metric
Mean
19
0
2
339
15
Marine
Water Use
Classifi-
EAR cation"
1.35d Class A
Od Class A
0.15 Class A
24. 2C Class A
1.11° Class A
Reference
URS (1986)
URS (1986)
U.S. EPA
(7 January 1988)c
URS (1986)
URS (1986)
a All entries are for fecal coliform bacteria concentrations in water samples except for the Priest Point
entry, which is for fecal coliform bacteria concentrations in shellfish.
Washington State standards for fecal coliform bacteria in the water column are defined in the text.
c Personal conmunication.
Inadequate number of samples to determine if 10 percent of the samples exceeded standard.
e More than 10 percent of the samples exceeded Washington State standards.
80
-------
PUGET
SOUND
m
*
*
- UNINVESTED TEO POTENTIAL
SCHJRCE OF FECAL COLJ FORM
BACTERIA
= NPDES-PERMfTTED DISCHARGES
[SEE TABLE 6)
= MARINA
•y
I I NOT SIGNIFICANT
• I SfflNFCAMT. < 10 X REFERENCE
•CD SIGNIFICANT. 10 - 50 X REFERENCE
^H SIGNIFICANT. > 50 X REFERENCE
INDICATES POOLED DATA AREA.
Figure 16. EAR values for concentrations of fecal coliform bacteria
in water samples from Budd Inlet.
-------
Additional fecal coliform bacteria data were summarized by URS (1986).
These data were collected at five point sources on five occasions. The San
Francisco storm drain and Ellis Creek contributed less than 3 percent of
the fecal coliform bacteria loading to Budd Inlet over the five sampling
periods. Moxlie Creek contributed the majority of the bacteria loading in
September 1984, April 1985, and June 1985. The major source of fecal
coliform bacteria in February 1985 was Capitol Lake, and the major source in
May 1985 was the LOTT WWTP.
Nonpoint sources of microbial contamination in Budd Inlet include
contributions from surface runoff from hobby farms, live-aboards in the five
Olympia marinas, and general boating activity. These contributions have not
been qualitatively or quantitatively identified.
CHEMICAL CONTAMINATION OF SEDIMENTS AND BIOTA
Chemical contamination of sediments and biota are discussed in the
following sections. The paucity of data precludes an overview of temporal
trends and detailed spatial trends. For selected indicators (i.e., sediment
contamination, bioaccumulation), data from recent studies were available to
help describe conditions.
Sediment Contamination
The physical and chemical characteristics of sediments in the Budd
Inlet study area are reviewed in the following sections.
General Overview—
Conventional Variables—Data on sediment total volatile solids (TVS)
and total organic carbon (TOC) are summarized in Figures 17 and 18. The
data are too limited to provide detailed characterization of any area in
Budd Inlet. Recently collected information is available only near the Port
of Olympia peninsula (in East and West Bays). Older data from Malins et al.
(1980) were collected from three stations in Budd Inlet (i.e., the south end
entrance channel, Priest Point, and Olympia Shoals). These data indicate
82
-------
03
OJ
• SAMPLING STATION
|f; | <2%TVS
2.1 TO 3% TVS
3.1 TO5%TVS
>5%TVS
OLYMPIA
CITY
BOUNDARY
I,-
4TH AVE.
OLYMPIA
Figure 17. Percent total volatile solids (TVS) measured in sediments at stations in the
East and West Bays of Budd Inlet.
-------
<2%TOC
2.1TO3%TOC
3.1TO5%TOC
>5%TVS
SAMPLING STATION
Figure 18. Percent total volatile solids (TVS) and percent total
organic carbon (TOG) measured in sediments at
stations in the East and West Bays of Budd Inlet.
84
-------
that TOC values at these stations have been similar to TOC values in recent
years. The most recent data on sediment grain size were collected by Mai ins
et al. (1980) and Westley et al. (1975). Data from Westley et al. (1975)
indicate that intertidal and subtidal sediments in the southern end of Budd
Inlet are largely silts and clays (approximately 91 percent). TVS content
of these sediments was approximately 10 percent. Data from Mai ins et al.
(1980) indicate that the subtidal sediments are primarily silt and clay.
The area near Priest Point appears to have a higher sand content than the
two other sampled areas. In general, the shallower areas are expected to
have coarser sediments and lower TOC than sediments in deeper areas.
Protected backwater areas and slips along the waterfront would be expected
to accumulate fine-grained, TOC-enriched sediments, but supporting data are
very limited. The available data indicate that lower concentrations of TOC
exist in intertidal sediments than in subtidal sediments, and that sediments
near the northern end of the Port of Olympia peninsula have TOC concen-
trations similar to concentrations in other areas of Puget Sound (see
Figures 17 and 18). No TOC data are available for any other areas of Budd
Inlet.
Toxic Chemicals—Past studies of toxic chemicals in the sediments of
Budd Inlet have been limited. Studies conducted prior to 1982 are considered
as historical studies for several reasons. First, the primary objective of
this report is to document current conditions in Budd Inlet. Second, the
LOTT WWTP began operation in August 1982. Changes in outfall location and
treatment efficiency could potentially alter contaminant loading. Third,
the precision of analytical methods has increased in the last 5 yr and data
comparable to data generated today were generally not available prior to
1982. Only three recent studies (Alan, R., 24 September 1987, personal
communication; Johnson, A., 22 July 1985, personal communication; Norton,
D., 5 February 1986, personal communication), discussed below, were of
acceptable quality to be used in the evaluation of sediment chemistry. The
geographic coverage of these studies is limited to the southern end of Budd
Inlet. Most areas of Budd Inlet, particularly north of Priest Point, have
not been sampled for sediment chemistry (Figures 19 and 20).
85
-------
00
Ol
•
A
•
*
SEDIMENT CHEMISTRY
WATER CHEMISTRY
SHELLFISH BIOACCUMULATION
SEDIMENT TOXICITY
OLYMPIA
CITY
BOUNDARY
4TH AVE.
OLYMPIA
Figure 19. Locations of sediment chemistry, water chemistry, shellfish bioaccumulation,
and sediment toxicity sampling stations in the East and West Bays of Budd Inlet,
1982-1987.
-------
• SEDIMENT CHEMISTRY
A WATER CHEMISTRY
• SHEU.RSH BIOACCUMULATION
NPDES OUTFALL
V IP*
J\B
SEEP
0 100 200
IFEET
n
Figure 20. Locations of sediment chemistry, water chemistry, and
shellfish bioaccumulation sampling stations at the
north end of the Port of Olympia peninsula.
87
-------
Limited sampling for sediment chemistry was conducted at three stations
in Budd Inlet by Malins et al. (1980) as part of a larger study that
documented the occurrence and fluxes of contaminants of special concern in
central and southern Puget Sound. Budd Inlet stations were located at the
entrance channel (southern end of inlet; Station 1), off Priest Point
(Station 2), and at Olympia Shoals (Station 3). Sediment samples at these
three stations were analyzed for petroleum hydrocarbons, PCBs, chlorinated
pesticides, other chlorinated organic compounds, and metals. Results of the
analyses indicated that Station 2 was the least impacted of the three
stations and exhibited low concentrations of most chemicals. Stations 1 and
3 exhibited higher concentrations of most chemicals, particularly arsenic,
copper, and HPAH. This was the only study that collected sediment chemistry
samples north of Priest Point (Station 3). Considerable additional sampling
is needed in this area to determine the extent of the chemical contamination.
The most recent available data indicate that the East Bay area near the
Cascade Pole Company facility, and the area near the West Bay storm drain
have elevated chemical concentrations in sediments. The number of chemicals
for which analyses were conducted in both of these areas was fewer than that
in many other areas of Puget Sound (e.g., Elliott and Commencement Bays), so
the full extent of any possible contamination cannot be established using
only the presently available data. The data from both areas indicate that
the problems are associated primarily with organic chemicals, and that
concentrations are among the highest observed in many other areas of Puget
Sound (e.g., Commencement and Elliott Bays) (Tetra Tech 1985a,b). From the
limited data available, it appears that concentrations of metals in sediments
near East and West Bays are similar to other areas of Puget Sound (Tetra
Tech 1985a,b). However, the area near the Fiddlehead Marina exhibited high
concentrations of cadmium in 1986 (Alan, R., 24 September 1987, personal
communication) which may indicate a potential problem exists there.
Available Data—A detailed analysis of sediment conditions between 1985
and 1986 was developed primarily from data reported in the following
documents:
88
-------
• Mr. R. Alan (24 September 1987, personal communication) and
Mr. F. Kessler (18 December 1987, personal communication)-
data from the LOTT WWTP Receiving Water Sampling Program
performed in 1986
• Mr. A. Johnson (22 July 1985, personal communication) - a
report on the nature and extent of creosote and pentachloro-
phenol in intertidal areas near Cascade Pole wood-treating
facility
• Mr. D. Norton (5 February 1986, personal communication) - a
report presenting results of U.S. EPA priority pollutant
analyses on water, sediment, and clam samples collected in
lower Budd Inlet near Cascade Pole wood-treating facility.
In addition to these data, 11 U.S. Army Corps of Engineers dredging permits
have been issued in the vicinity of Budd Inlet since 1980. Information on
these permits, which include identification of contaminated sediments that
were dredged from Budd Inlet, is summarized in Appendix C.
These studies represent all recent data that provide information on at
least one of the indicator chemicals. Field collections of the selected
data were conducted in 1985. In general, data from these studies were
supported by quality assurance/quality control (QA/QC) programs, and the
methods used to measure contaminant concentrations were appropriate.
Results of the data evaluations for all studies, and a summary of the
sampling intensity and variables measured from these accepted documents are
shown in Appendix A, Tables A-3 and A-7.
Data Synthesis--
Choice of Indicators—About 50 organic compounds and metals have been
measured in sediments collected in Budd Inlet. These chemicals include many
of the trace metals that are considered toxic, and representative compounds
from nearly all the major types of toxic organic substances (see Table 2).
Many of the chemicals were detected at levels near the limits of the
89
-------
analytical procedures, and were found in relatively few of the sediment
samples. Also, in some of the studies, substances were not measured
accurately or with sufficient sensitivity. Therefore, only data for
selected chemicals are discussed below. The following chemical indicators
were used to establish the level of sediment contamination:
• Sum of LPAH
• Sum of HPAH
• Sum of concentrations of copper, lead, and zinc
• Cadmium
• Arsenic.
Concentrations of related substances were summed when the individual
chemicals were found to strongly covary in their distributions in the
sediments. The composite indicators (i.e., LPAH, HPAH, sum of copper, of
lead, and of zinc) were found to be reasonable surrogates for a broad range
of individual substances with similar distributions in the system. They
also represent a range of sources and transport mechanisms. Finally, the
composite indicators are known to cause toxic responses in organisms under
laboratory conditions.
Table 8 shows the data limitations of the selected studies discussed
above. Not all composite indicator substances were measured at all stations
sampled during these studies.
Station Locations—Station locations for the selected studies are given
in Figures 19 and 20. A nonuniform allocation of sampling efforts is
obvious. Most areas of Budd Inlet have received almost no study, while
other areas (e.g., East and West Bays) have been sampled with greater
intensity. Such spatial heterogeneity makes it difficult to distinguish
spatial trends in contaminant concentrations.
90
-------
TABLE 8. DATA LIMITATIONS OF SELECTED STUDIES USED
IN DETAILED ANALYSIS OF SEDIMENT CHEMISTRY
Conventi onals
Study TOC TVS
Alan
(24 September 1987)
Johnson
(22 July 1985)a
Norton
(5 February 1986) a
Nob
a
Yes
Yes
Yesc
No
No
LPAH
NAd
Ace
Ace
Chemicals
HPAH PCB
NA
Ace
Ace
NA
NA
NA
Analyzed
Cu+Pb+Zn
Acce
NA
(Copper)
NA
As
NA
Ace
NA
a Personal communication.
b No = Not sampled or analyzed.
c Yes = Sampled and analyzed.
d NA = Not Analyzed.
e Ace = Acceptable data.
91
-------
Reference Area Data—The ranges of sediment concentrations of metals and
organic compounds for up to nine Puget Sound reference areas are summarized
in Tables 9 and 10. It is assumed that this range of reference concentra-
tions provides a reasonable measure of the variability of concentrations in
relatively uncontaminated sediments (Tetra Tech 1985b,c). The full range of
Puget Sound reference area data (collected from 1979 to 1985) is used to
determine whether EAR values are significant (i.e., whether the contamination
exceeds all Puget Sound reference conditions). This approach was success-
fully used to evaluate EAR significance in Elliott Bay and Everett Harbor
(Tetra Tech 1985b,c).
The reference area data used to calculate EAR values were a subset of
the full Puget Sound reference data. Data from six Carr Inlet stations
sampled in 1984 were averaged and used to calculate EAR conditions for the
following reasons:
• The most complete reference data set is available for Carr
Inlet and it includes synoptic data for metals, organic com-
pounds, grain size, organic carbon, and other conventional
variables
• The lowest reference detection limits for most substances of
concern in Puget Sound embayments are available for Carr
Inlet
• EAR values for other urban embayments (e.g., Elliott Bay,
Everett Harbor, Commencement Bay) have been calculated using
the data, and therefore, will be directly comparable with EAR
values for Budd Inlet
• Chemical concentrations for samples analyzed from Carr Inlet
were comparable to or lower than concentrations in other
reference areas, and therefore, appear to be reasonably
representative of Puget Sound reference conditions.
92
-------
TABLE 9. SUMMARY OF METAL CONCENTRATIONS IN
SEDIMENTS FROM PUGET SOUND REFERENCE AREAS
Range
Antimony
Arsenic
Beryllium
Barium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Silver
Thallium
Zinc
(mg/kg
U O.lb
1.9
0.07
5.6
0.1
9.6
5
U 0.1
0.01
4
U 0.1
0.02
U 0.1
15
dry wt)
- 1.7
- 17
- 5.5
- 7.8
- 1.9
- 130
- 74
- 24
- 0.28
- 47
- 1.0
- 3.3
- 0.2
- 100
Mean
(mg/kg dry wt)
0.32C - 0.38d
7.2
2.3
6.9
0.67
54
32
9.8C - 9.8d
0.08
28
0.36C - 0.62d
1.2
0.05C - 0.12d
62
Detection
Frequency
12/32
34/34
26/26
4/4
24/24
38/38
28/28
21/28
38/38
26/26
16/24
26/26
8/22
26/26
Reference
Sites3
1,2,3,4,7,8,9
1,2,3,4,7,8,9
1,2,3,4,5,9
1
1,2,3,4,6,9
1-9
1,2,3,4,5,6,9
1,2,3,4,5,6,9
1-9
1,2,3,4,5,9
1,2,3,4,6,9
123459
1 , C. , ~> , ~t ,
-------
TABLE 10. SUMMARY OF ORGANIC COMPOUND CONCENTRATIONS
IN SEDIMENTS FROM PUGET SOUND REFERENCE AREAS
Substance
Phenol s
65 Phenols
HSL
HSL
34
2-methyl phenol
4-methyl phenol
2,4-dimethylphenol
Range
(ug/kg dry wt)
U 10
62b
Mean
(ug/kg dry wt)
c
37d
U 10
U 10
U 1
32
U 10
14
—
20
Detection
Frequency
3/13
0/4
2/4
0/6
Reference
Sites3
1,2,3
--
1
1
Substituted Phenols
24
31
22
21
HSL
64
57
59
60
58
2-chlorophenol
2 , 4-di chl orophenol
4-chl oro-3-methyl phenol
2, 4, 6-tri chl orophenol
2,4, 5-tri chl orophenol
pentachl orophenol
2-nitrophenol
2,4-dinitrophenol
4 , 6-di ni tro-o-cresol
4-nitrophenol
U 0.5
U 0.5 •
U 0.5
U 0.5
U 5
- U 10
U 10
U 10
—
—
--
—
U 10
0.1
0.1
U 0
U 0.5
U 0.5 -
U 50
U 10
.5
U 100
U 100
0.02
—
—
—
—
33
0/6
0/6
0/6
0/6
0/4
1/6
1/6
0/6
0/6
0/6
1
1
1
1
1
1
1
1
1
1
Low Molecular Weight Polynuclear Aromatic Hydrocarbons
55
77
1
80
81
78
HSL
High
39
84
72
76
74
75
73
83
82
79
naphthalene
acenaphthylene
acenaphthene
fluorene
phenanthrene
anthracene
2-methyl naphthalene
Molecular Weight Polynuclear
fluoranthene
pyrene
benzo(a)anthracene
chrysene
benzo ( b ) f 1 uoranthene
benzo (k) fl uoranthene
benzo (a) pyrene
i ndeno( 1 , 2 , 3-c , d) pyrene
di benzo (a, h) anthracene
benzo(g,h,i )perylene
U 0.5
U 0.1
U 0.1
U 0.1
5
U 0.5
1
U 40
U 40
U 40
40
170
U 40
20
5.6 -
0.08 -
0.48
3.0
19
2.7
7.5
22
• 17
17
19
35
22
9.5
10/20
1/20
4/20
7/21
11/17
7/17
6/10
1,2,3,4,5,
1,2,3,4,5,
1,2,3,4,5,
All
1,2,3,6,7
1,2.3,6,7
1,4,5,6
6
6
6
Aromatic Hydrocarbons
7
8
100
120
4 - U 40
U 5
U 5
U 5 -
U 0.37
U 0.37
0.4 -
3
U 40
94
- 94
40
30
U 5
20
32
30
3.7
6.4
17 -
17
9.3 -
7.4 -
0.08 -
3.8
41
41
23
26
33
33
10
9.2
4.1
7.2
17/22
16/22
8/17
8/17
12/21
12/21
10/14
6/12
1/5
2/6
All
All
1,2,3,6,7
1,2,3,6.7
All
All
1,3,4,5,6,
1,4,5,6,7
1
1,7
7
Chlorinated Aromatic Hydrocarbons
26
27
25
8
20
9
1 , 3-di chl orobenzene
1 , 4-di chl orobenzene
1 , 2-di chl orobenzene
1 , 2 , 4-t ri chl orobenzene
2-chl oronaphthal ene
hexachl orobenzene (HCB)
U 0.06
U 0.06
U 0.06
U 0.5
U 0.5
0.01
U 40
- U 40
U 40
- U 5
U 50
U 10
0.004
0.004
0.004
--
--
0.07
19
19
- 19
3.5
1/18
1/18
1/18
0/6
0/6
6/12
1,2.3,4,E
1,2,3,4,5
1,2,3,4,5
1
1
1,4,5,6
Chlorinated Aliphatic Hydrocarbons
12
XX
XX
XX
52
53
hexachl oroethane
trichlorobutadiene
tetrachlorobutadiene Isomers
pentachl orobutadi ene isomers
hexachl orobutadi ene
hexachl orocycl opentadi ene
U 0.5
U 0.03
U 0.04
0.03 -
U 0.03
U 50
U 25
- U 25
U 25
- U 25
—
0.27
1.6 -
0.15
0.07 -
7.9
9.2
7.7
8.5
0/6
5/12
5/12
5/12
5/12
1
1,4,5,6
1,4,5,6
1,4,5,6
1.4,5,6
not analyzed
94
-------
TABLE 10. (Continued)
Halogenated Ethers
18 bis(2-chloroethyl) ether
42 bis(2-chloroisopropyl ) ether
43 bis(2-chloroethoxy)methane
40 4-chlorophenyl phenyl ether
41 4-bromophenyl phenyl ether
Phthalate Esters
71 dimethyl phthalate
70 di ethyl phthalate
68 di-n-butyl phthalate
67 butyl benzyl phthalate
66 bis(2-ethylhexyl)phthalate
69 di-n-octyl phthalate U 0,
Miscellaneous Oxygenated Compounds
54 i sophorone
HSL benzyl alcohol
HSL benzoic acid
129 2,3,7, 8-tetrachl orodi benzo-p-
dioxin
HSL dibenzofuran
Organonitrogen Compounds
HSL aniline
56 nitrobenzene
63 n-nitroso-di-n-propylamine
HSL 4-chloroaniline
HSL 2-nitroaniline
HSL 3-nitroaniline
HSL 4-nitroaniline
36 2,6-dinitrotoluene
35 2,4-dinitrotoluene
62 n-nitrosodi phenyl ami ne
37 1,2-di phenyl hydrazine
5 benzidine (4,4'-diamino-biphenyl)
28 3,3'-dichlorobenzidine
Pesticides
93 p,p'-DDE
94 p.p'-DDD
92 p,p:-DDT
89 aldrin
90 dieldrin
91 chlordane
95 alpha-endosulfan
96 beta-endosulfan
97 endosulfan sulfate
98 endrin
99 endrin aldehyde
100 heptachlor
101 heptachlor epoxide
102 alpha-HCH
103 beta-HCH
104 delta-HCH
105 gamma-HCH (lindane)
113 toxaphene
PCBs
xx Total PCBs (primarily 1254/1260)
0.3 U 10
U 0.5 U 10
U 10
U 0.5 US
U 0.5 U 5
U 0.5 U 50
9.0 11
U 20 760
U 0.5 U 25
U 0.5 U 25
.5 U 25
U 0.5 U 130
U 10
U 25 - 430
not analyzed
U 5
U 1.0 U 20
U 0.5 U 5
U 0.5 U 10
U 50
U 50
U 50
U 50
U 0.5 U 10
U 0.5 U 5
U 0.5 US
U 0.5 U 5
U 0.5
U 0.5 U 100
U 10 U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10 - U 25
U 10 - U 25
U 10 U 25
U 10 - U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10 U 25
U 10
3.1 U 20
1/4
0/6
0/6
0/6
0/6
0/5
4 8 4/5
160 170 3/5
0/5
0/5
0/5
0/5
0/4
210 216 3/4
0/4
0/6
0/5
0/5
0/4
0/4
0/4
0/4
0/5
0/5
0/5
0/6
0/2
0/6
0/5
0/6
0/5
0/6
0/6
0/6
0/5
0/5
0/5
0/6
0/5
0/6
0/6
0/6
0/6
0/6
0/6
0/2
1.8 12 7/19
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1,2,3,4,6,7
95
-------
TABLE 10. (Continued)
Volatile Compounds
85
38
tetrachloroethene
ethyl benzene
U 4,
U 4,
,1 U 16
,1 U 16
0/8
0/8
2,3
2,3
a
Reference sites: 1. Carr Inlet
2. Samish Bay
3. Dabob Bay
4.
5.
6.
Carr Inlet
Port Madison
Port Susan
7. Nisqually Delta
" An anomalously high phenol value of 1800 ug/kg dry weight was found at one Carr Inlet station. For the
purpose of reference area comparisons, this value has been excluded.
c Mean calculated using 0.00 for undetected values.
" Mean calculated using the reported detection limit for undetected values.
Reference:
(Site 1) Tetra Tech (1985a); Mowrer et al. (1977).
(Site 2) Battelle Northwest (1983).
(Site 3) Battelle Northwest (1983); Prahl and Carpenter (1979).
(Site 4) Mai ins et al. (1980); Mowrer et al. (1977).
(Site 5) Malins et al. (1980).
(Site 6) Malins (1981).
(Site 7) Barrick and Prahl (in review); Mowrer et al. (1977).
96
-------
The Carr Inlet samples collected in 1984 provide the most comprehensive
reference data for Puget Sound. These data include blank-corrected analyses
for 13 U.S. EPA priority pollutant metals, 3 additional metals (including
iron and manganese as natural indicators), 78 U.S. EPA extractable priority
pollutant compounds, 12 additional U.S. EPA Hazardous Substance List
compounds, and selected tentatively identified compounds. Data for almost
all of the organic compounds were corrected for potential losses during
sample preparation and analysis using isotope mass spectroscopy. The
comprehensive nature of these data is a major reason for their sole use in
calculating elevations above reference values.
The most commonly analyzed contaminants in other reference areas (see
Tables 9 and 10) were metals and neutral organic compounds (especially
hydrocarbons). With the exception of selected hydrocarbon data from the
Nisqually River delta and Dabob Bay, analytical recovery data were not
available for evaluation of the organic compound data from the other
reference data sets. Phthalate data were available for some of the other
reference areas, but were rejected because the data apparently were not
corrected for potential laboratory contamination, a common problem with this
group of compounds.
Detection limits for some reference areas exceeded 50 ug/kg dry weight
for several organic compounds. Detection limits for the recent Carr Inlet
samples ranged from 0.5 to 50 ug/kg dry weight for almost all compounds. To
provide a comparable data set, a maximum detection limit of 50 ug/kg dry
weight was set for the acceptance of data from other reference areas
included in the ranges reported in Table 10. For the few reference data
sets affected by this cutoff, most of the relevant compounds have either
been found at levels below 50 ug/kg dry weight, or have been undetected at
low concentrations in the remaining reference areas. This cutoff makes the
determination of the significance of Budd Inlet contamination less sensitive
to limitations of analytical methods and more sensitive to the actual levels
of compounds in reference areas.
Elevations Above Reference (EAR) Analysis—Dry weight concentrations of
selected chemical indicators in the sediments of Budd Inlet were divided by
97
-------
the average concentration for those indicators measured in sediments of the
Carr Inlet reference area. Detailed spatial distributions of the EAR values
for selected indicators are presented in Figures 21-26.
The calculated EAR values for the selected indicators are presented by
station in Table 11. Of the selected indicators, the organic compounds
(i.e., LPAH and HPAH) exhibited much higher EAR values than did the metals.
EAR values for LPAH and HPAH exceeded 100 at most stations, while those for
metals rarely exceeded 3. Specific characteristics of East and West Bays
are discussed below.
The intertidal area in East Bay near the Cascade Pole Company facility
exhibited the highest elevations for all indicator chemicals in the project
area. EAR values for both LPAH and HPAH exceeded 50 at all stations. These
chemical elevations were all above the significance level (i.e., the
concentrations were greater than the highest concentrations observed in any
reference area in Puget Sound; Tetra Tech 1985a,b). Concentrations of LPAH
and HPAH at Station 2 were much higher than those noted in other contaminated
areas of Puget Sound (Tetra Tech 1986b) (see Table 11). EAR values for LPAH
and HPAH were highest in intertidal sediments at Stations 1-3 and tended to
decrease in subtidal areas (see Table 11). Possible sources of contaminants
that caused these high concentrations are multiple seeps that occur in East
Bay (White, M., 21 January 1988, personal communication). Arsenic concentra-
tions were fairly typical of other nonreference areas in Puget Sound (Tetra
Tech 1985a,b). The associated EAR values did not exceed 3 (see Table 11).
Data for other indicator chemicals were not collected.
Contaminant concentrations in sediment and associated EAR values near
the West Bay storm drain, which is in contact with contaminated groundwater
beneath Cascade Pole Company site varied (Johnson, A., 22 July 1985, personal
communication). EAR values for LPAH and HPAH were highest at the intertidal
station located just south of the outfall, while the intertidal station to
the north of the outfall had the lowest EAR values for LPAH and HPAH. The
subtidal station exhibited intermediate concentrations. Actual concentra-
tions were much lower than the highest values reported for stations in East
98
-------
100
200
SAMPLING STATION
NOT SIGNIFICANT
SIGNIFICANT, < 10 X REFERENCE
SIGNIFICANT, 10 -100 X REFERENCE
SIGNIFICANT, 100 -1000 X REFERENCE
SIGNIFICANT, > 1000 X REFERENCE
Figure 21. EAR values for concentrations of LPAH in sediments
from the East and West Bays of Budd Inlet.
99
-------
• SAMPLING STATION
I I NOT SIGNIFICANT
SIGNIFICANT, < 10 X REFERENCE
SIGNIFICANT, 10 -100 X REFERENCE
SIGNIFICANT, 100-1000 X REFERENCE
SIGNIFICANT, > 1000 X REFERENCE
Figure 22. EAR values for concentrations of HPAH in sediments
from the East and West Bays of Budd Inlet.
100
-------
SAMPLING STATION
NOT SIGNIFICANT
SIGNIFICANT, < 10 X REFERENCE
SIGNIFICANT. 10 - 50 X REFERENCE
--/i
-OLYMPIA
CITY
BOUNDARY
4TH AVE.
OLYMPIA
Figure 23. EAR values for concentrations of copper, lead, and zinc in sediments from the
East and West Bays of Budd Inlet.
-------
•cm
SAMPLING STATION
NOT SIGNIFICANT
SIGNIFICANT. < 10 X REFERENCE
SIGNIFICANT, 10 - 50 X REFERENCE
100
200
I FEET
Figure 24. EAR values for concentrations of copper, lead, and
zinc in sediments from the East and West Bays of
Budd Inlet.
102
-------
o
u>
• SAMPLING STATION
| | NOT SIGNIFICANT
SIGNIFICANT, < 10 X REFERENCE
OLYMPIA
CITY
BOUNDARY
I.-
4TH AVE
OLYMPIA
Figure 25. EAR values for concentrations of cadmium in sediments from the East and West
Bays of Budd Inlet.
-------
• CZI
POflT //
DETENTION
BASIN
• SAMPLING STATION
I I NOT SIGNIFICANT
SIGNIFICANT, < 10 X REFERENCE
100
200
iFEET
Figure 26. EAR values for concentrations of arsenic in sediments
from the East and West Bays of Budd Inlet.
104
-------
TABLE 11. CONCENTRATIONS AND EAR VALUES FOR SELECTED CHEMICAL INDICATORS IN BUDD INLET3
Area
East Bay
(Intertidal)
ii n
ii i
u i
n
East Bay
(Offshore)
n n
Area Average
West Bay
Outfall
(Intertidal)
i— > M n
o
tn
"
West Bay
Outfall
(Subtidal)
n n
Capitol Lake
Outfall
Fiddlehead
Marina
Area Average
Station
1
2
3
4
5
6
7
8
338035
338034
338036
3
1
2
LPAH
Conc.b
48,800 1
1,745,000 42
22,540
9,060
12,640
5,180
1,702
263,560 6
f
210
6,100
880
--
--
--
2,397
EAR
,198*
*
.833
553*
222
310*
127*
42
,469*
f
5
*
150
27
--
--
--
59*
HPAH
Conc.b
75,100
1,258,000 15
95,800 1
10,150
4,240
15,500
14,080
210,410 2
880
1,300
16,000
3,200
--
--
5,345
Cu+Pb+Zn As Cd
EAR Conc.c EAR Conc.c EAR Conc.c EAR
954* -d -- 8.0 2
,985 -- -- 5.7 2
,217* -- -- 10.7 3
129 -- -- 11.0 3
54* -- -- 5.5 2
197* -- -- 7.6 2
179 -- -- 7.3 2
,674* 8.0 2
11* -- -- 9.0 3
17
*
203
41
165.5 4.8 0 0
38.5 1.1 0 0
256.3 7.4 -- -- 5.6 5.9
68* 153.4 4.4 1.9 2.0
LPAH
2
1
3
5
4
6
7
f
3
1
2
--
--
--
EAR RANK3
HPAH Cu+Pb+Zn As
3 e
1
2
6
7
4
5
4
3
1
2
2
3
1
Cd
--
--
--
--
--
..
--
_-
--
--
--
e
e
(1)
a Asterisk indicates significant EAR (i.e., chemical concentration in study area is greater than the maximum value observed in all Puget Sound reference areas; Tetra
Tech 1986b).
Concentration = ug/kg.
c Concentration = mg/kg.
d No data collected.
e Since none of the EAR values were significant, they were not ranked.
f All LPAH compounds were undetected with a detection limit of 100 ug/L at this station.
-------
Bay, however, all EAR values were significant when compared with Puget Sound
reference areas.
Other areas in West Bay were only sampled for metals. The composite
indicator for copper, lead, and zinc exhibited a significant EAR for
sediments near the Fiddlehead Marina. In addition, the cadmium concentration
in sediments from a station near Fiddlehead Marina exhibited significant EAR
values. The lack of data in the remaining areas of West Bay and Budd Inlet
does not allow for a comprehensive discussion of sediment contamination.
Comparison to Apparent Effects Threshold (AET) Values—The AET values
were used to identify concentrations of specific contaminants in sediments
above which biological concentrations of specific contaminants in sediments
above which biological effects are expected to occur. AET values are based
on sediment chemistry data, toxicity data (i.e., amphipod, oyster larva, and
Microtox bioassays), and benthic infauna abundance. For a given chemical
and a specified biological indicator, the AET is the concentration above
which statistically significant biological effects occurred in all samples
of sediments analyzed. Because of limited biological (e.g., benthic
infauna, bioassay) data in Budd Inlet, contaminant concentrations in budd
Inlet sediments have been compared to these Puget Sound AET values to
predict potentially significant biological effects. The range and mean of
each chemical detected in sediments from lower Budd Inlet can be compared
to AET values in Table 12. Raw data are provided in Appendix D.
j
The minimum concentrations of all organic and inorganic chemicals were
below the lowest AET (LAET) values in all cases except the following: 2,4-
dimethylphenol, 2-methylphenol, 1-methylnaphthalene, dibenzothiophene, and
biphenyl. The maximum concentrations of all organic compounds exceeded the
LAET values except for acenaphthylene, benzo(g,h,i)pyrelene, dibenzo(a,h)an-
thracene, indeno(l,2,3-cd)pyrene, 4-methylphenol, and phenol. The maximum
concentration of chromium exceeded its LAET value./ The maximum concentra-
tion of cadmium (5.6 mg/kg) is similar to the LAET for cadmium (5.8 mg/kg).
Cascade Pole is the most likely source of these contaminants.
106
-------
TABLE 12. COMPARISONS OF CONTAMINANT CONCENTRATIONS3 IN BUDD INLET SEDIMENTS WITH PUGET SOUND AET VALUES
Budd Inlet Data
Class
LPAH
HPAH
TPAH
Phthalates
Phenol s
Miscellaneous Extractables
Volatile Organics
Metal s
Chemical
acenaphthene
acenaphthylene
anthracene
fluorene
naphthalene
phenanthrene
benzo (a ) anthracene
benzo(a)pyrene
benzo(g,h,i Jperylene
benzof 1 uoranthenes
chrysene
di benzo(a . h)anthracene
fluoranthene
i ndeno( 1,2, 3-cd)pyrene
pyrene
Total PAH
bis(2-ethy1hexyl )phthalate
2, 4-dimethyl phenol
2-methyl phenol
4 -methyl phenol
pentachl orophenol
phenol
1-methyl naphthal ene
2-methyl naphthal ene
biphenyl
dibenzofuran
dibenzothiophene
ethyl benzene
total xyl enes
arsenic
cadmium
chromium
copper
lead
mercury
nickel
zinc
N
12
12
12
12
12
12
12
12
12
12
12
4
12
12
12
4
8
8
8
8
12
8
3
15
3
12
3
8
8
8
3
11
11
3
1
3
3
Mean
32,844
175
13.500
17,398
19,961
69,221
9.876
3,822
156
7,764
12,134
93
52,414
156
38,682
7,370
2,468
188
188
190
156
188
261,633
1.533
725
11,559
270,000
76
55
8.1
1.9
31.6
63.7
16.4
0.2
23.1
86.1
Min
20
20
20
20
39
100
20
20
20
50
20
20
220
20
450
880
100
100
100
100
20
100
2,100
20
540
20
270,000
5
5
5.5
0.0
3.7
0.0
6.5
0.2
2.7
29.3
Max
370,000
400
150,000
200,000
210,000
800,000
95,000
40,000
400
73,000
120,000
200
530,000
400
400,000
23,000
15,000
400
400
400
400
400
780,000
15,000
910
130,000
270,000
510
400
11.0
5.6
55.6
131.5
33.4
0.2
41.7
116.9
Puqet
Amphipod
980
560
1,900
1.800
2,400
5,400
3,000
2,400
960
3,700
5,000
510
9,800
880
11,000
> 3,100
> 72
63
1,200
> 140
670
310
670
260
540
240
> 50
> 160
93
6.7
> 130
800
700
2.10
> 120
870
Sound Aooarent Effects Threshold
Oyster
500
> 560
960
540
2.100
1,500
1,600
1.600
720
3,600
2,800
230
2.500
690
3,300
1,900
29
63
670
> 140
420
370
670
260
540
240
37
120
700
9.6
> 37
390
660
0.59
39
1,600
Benthic
500
640
1,300
640
2,100
3,200
4,500
6,800
5,400
8,000
6,700
1,200
6.300
- 5,200
> 7,300
1,900
29
> 72
670
> 140
1,200
370
670
270
540
250
37
120
85
5.8
59
310
300
0.88
49
260
Microtox
500
> 560
960
540
2,100
1,500
1,300
1,600
670
3.200
1,400
230
1.700
600
2,600
1,900
29
> 72
670
> 140
1,200
370
670
270
540
250
33
100
700
9.6
27
390
530
0.41
28
1.600
(AET) Valuesb
LAET
500
560
960
540
2,100
1,500
1,300
1.600
670
3.200
1,400
230
1,700
600
2,600
1,900
29
63
670
420
310
670
260
540
240
33
100
85
5.8
27
310
300
0.41
28
260
HAET
980
640
1,900
1,800
2,400
5,400
4,500
6,800
5,400
8,000
6,700
1,200
9,800
880
11.000
1,900
29
63
1,200
1,200
370
670
270
540
250
37
120
700
9.6
59
800
700
2.10
49
1,600
a Concentrations of organic contaminants expressed in units of ug/kg dry wt, and concentrations of trace metals expressed in units of mg/kg dry wt.
b LAET=lowest AET; HAET=highest AET; >=actual AET value is greater than the value shown and threshold value has not been determined.
Reference: Adapted from: Alan, R. (24 September 1987, personal communication); Norton, D. (5 February 1986, personal conmunication); and Johnson, A. (22 July
1985, personal communication).
-------
Bloaccumulation
General Overview--
Bioaccumulation data collected since December 1981 for marine organisms
in Budd Inlet are limited to the concentration of PAH in tissues of clams
from four stations (see Figures 19 and 20). In the sample of clams collected
in East Bay near the Cascade Pole Company facility, the concentrations of PAH
were at the upper end of concentrations reported in other Puget Sound urban
bays (i.e., 1,100 ug/kg total PAH), and were similar to concentrations
detected in Eagle Harbor clams (Norton, D., 5 February 1986, personal
communication). Concentrations of total PAH (99 and 190 ug/kg) in clams
from West Bay were approximately an order of magnitude lower than those
observed in East Bay. PAH were undetected in clams collected at Priest
Point.
In 1986 and 1987, DSHS (1987) analyzed clam tissues from Priest Point
Park for heavy metals and selected organic compounds. Because of quality
assurance issues, these data were not made available in time to be incor-
porated into this report.
Because of the limited recent bioaccumulation data, older data (i.e.,
Mai ins et al. 1980) are included to provide an indication of the concentra-
tions of contaminants detected in bottomfish. In 1979, elevated concentra-
tions of some metals were found in liver tissues of English sole collected
from Budd Inlet (Maiins et al. 1980). However, specific station locations
for these data were not presented. Concentrations of strontium in liver
tissues of English sole from Budd Inlet were reportedly 39 times greater
than concentrations detected in Sinclair Inlet, 17 times greater than
concentrations detected along the Elliott Bay waterfront, and 25 to 31 times
greater than concentrations detected in Hylebos Waterway. Strontium is not
considered toxic (Maiins et al. 1980). However, these elevations in English
sole liver tissue suggest a source of strontium in Budd Inlet. Calcium was
also elevated by over an order of magnitude compared to concentrations in
fish livers collected from Case and Sinclair Inlets, Duwamish River, Seattle
108
-------
Waterfront, and Hylebos and Sitcum Waterways. Naphthalene, acenaphthalene,
dichlorobenzene, and trichlorobutadiene in composite samples containing
English sole livers collected throughout Budd Inlet appeared elevated in
comparison with Port Madison, Case Inlet, and Sinclair Inlet. However,
because detection limits were not reported, these results should be inter-
preted with caution.
Data Synthesis —
An analysis of bioaccumulation data collected since 1982 will be used
to define toxic contamination problems in the study area. The following
analysis deviates from the traditional action assessment approach used in
other urban embayments (e.g., Elliott Bay, Everett Harbor), because bioac-
cumulation data exists for clams only. Although one station in Budd Inlet
was considered a reference station by Mr. D. Norton (5 February 1986,
personal communication), all contaminants were undetected in the sample from
that station. However, the detection limits in that study were higher than
detection limits used in other recent bioaccumulation studies.
Available Data—Recent data on priority pollutant concentrations in
clam tissues were compiled from Mr. D. Norton (5 February 1986, personal
communication). These were the only data available for the study period
1982-1987.
Choice of Indicators—Chemical indicators chosen for analysis of
bioaccumulation in clam tissues were:
• Sum of LPAH
• Sum of HPAH.
These indicators represent a subset of the chemicals that are usually
investigated in tissue samples. Data on PCBs and metals were not available,
and are needed to identify the biological effects that may be induced by
these environmental contaminants.
109
-------
Station Locations—Two stations were located near the West Bay storm
drain outfall and one station was located near the Cascade Pole Company
facility (see Figure 20). A reference station was located near Priest Point
(see Figure 19).
Reference Area Data—Reference concentrations of LPAH and HPAH in
clams were obtained from the Puget Sound Environmental Atlas (Evans-Hamilton
and D.R. Systems 1986). These reference data use a compilation of data from
Mai ins et al. (1980) and Yake et al. (1984). The database from which
reference values for bioaccumulation of contaminants in clams is determined
is limited since bioaccumulation is traditionally investigated in bottom-
dwelling fish and crabs.
EAR Analvsis—Bioaccumulation data for clams are summarized in Table
13. Metals were not included in the analyses. However, 10 organic priority
pollutants were identified in the clams that were collected from near the
Cascade Pole Company. A total of six LPAH and ten HPAH compounds were
analyzed. Acenaphthylene was the only undetected LPAH compound. Of the
HPAH, benzo(a)pyrene, dibenzo(a,h)anthracene, indeno(l,2,3-cd)pyrene, and
benzo(g,h,i)perylene were undetected.
Bioaccumulation of LPAH and HPAH was greatest at the station off the
Cascade Pole facility in East Bay. Concentrations of LPAH and HPAH were
169 and 938 ug/kg wet weight, respectively. These values fall within the
range of values observed from Eagle Harbor. EAR values were 5.0 for LPAH
and 12.3 for HPAH. Bioaccumulation in clams collected at the two stations
near the West Bay drain were 27 and 83 ug/kg (wet wt) for total LPAH and 72
and 110 ug/kg (wet wt) for total HPAH. These values are similar to lower
values obtained from other urban embayments in Puget Sound (Norton, D., 5
February 1986, personal communication).
The limited data available for analysis of bioaccumulation in Budd
Inlet suggest that PAH are accumulating to abnormally high levels in clams
in the vicinity of Cascade Pole Company. The earlier data by Mai ins et al.
(1980) suggest the bioaccumulation of strontium and calcium in abnormally
high concentrations. Until further studies are conducted, the significance
110
-------
TABLE 13. SUMMARY OF BIOACCUMULATION DATA FOR BUDD INLET
Sample Type
Clamsc
Station
Priest
Point
East
Bay
West Bay
Drain-1
West Bay
Drain-2
na
31
11
27
27
LPAH HPAH
Concentration*3 EAR Concentration15
169 5.0 938
83 2.4 108
27 0.8 72
EAR
12.3
1.4
0.9
a n = number of clams composited into one sample.
b Concentration is expressed in ug/kg wet weight.
c Protothaca staminea. Tapes .iaponica. and Mva arenaria.
Reference: D. Norton (5 February 1986, personal communication).
Ill
-------
of these elevations can not be ascertained. Acenaphthylene was the only LPAH
undetected in all tissue samples. Benzo(a)pyrene, dibenzo(a,h)anthracene,
indeno(l,2,3-cd)pyrene, and benzo(g,h,i)perylene were undetected in all
tissue samples.
Toxicity Bioassavs
Bioassays are conducted to test organism response to bioavailable toxic
substances in contaminated effluent and sediments. Presently, this cannot be
determined by routine chemical analytical techniques. Therefore, bioassays
should be used in conjunction with chemical data when characterizing
ecological impacts of contaminated sediments or water on organisms. Three
types of bioassays are used to test receiving water toxicity, sediment
toxicity, and effluent toxicity. Simultaneous consideration of benthic
infaunal community, chemistry, and bioassay data is effective for conducting
site-specific analysis of conditions in the sedimentary environment (Tetra
Tech 1985b,c; Long and Chapman 1985).
Overview--
Receiving water bioassays were conducted during 1973-1976 at six
stations in Budd Inlet. Recent data are not available. Two types of
sediment bioassays (i.e., amphipod and oyster larva) were performed on
sediments collected in March 1985 at a single station in Budd Inlet.
Effluent bioassays are not a component of the NPDES permit requirements for
the LOTT WWTP (Alan, R., 9 February 1988, personal communication).
Receiving Water Toxicitv—Receiving water bioassays were not conducted
in Budd Inlet during the study period for this report (i.e., 1982-1987).
However, receiving water bioassays were conducted during the period 1973-
1976 at six stations (Washington Department of Fisheries 1979). The six
stations were located in central Budd Inlet near Gull Harbor, south of Gull
Harbor, near Butler Cove, near Priest Point, near the old LOTT outfall
(i.e., approximately 100 yd off Fiddlehead Marina), and at the Port of
Olympia docks near the head of West Bay. No stations were located in East
Bay. Water samples were collected at the surface and at various depths in
112
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the water column. Oyster larvae (Crassostrea qiqas) bioassays were conducted
on each of the samples. Sample collection methods and laboratory QA/QC
procedures were adequate and included the use of a reference toxicant.
At all stations, percent abnormality and percent mortality showed
considerable variability. Percent mortality was generally higher than
percent abnormality, except near the LOTT outfall where these values were
approximately equal. Percent abnormality and percent mortality ranged
between 0 and 100 percent at stations located south of Gull Harbor, and near
Butler Cove, Priest Point, and the LOTT outfall. Percent abnormality and
percent mortality were generally lower at the Port of Olympia docks than at
other stations in Budd Inlet; values from the station near the Port of
Olympia docks were similar to those from stations sampled near Dana Passage
and Ketron Island.
Sediment Toxicity—Two types of sediment bioassays have been performed
in Budd Inlet. The Rhepoxynius abronius sediment bioassay, developed by
Swartz et al. (1985), was used for bioassays conducted on sediment from one
station located north of the Port of Olympia peninsula, and on sediment
collected at the Olympia Yacht Club (see Figure 19). The oyster larvae
(Crassostrea giqas) bioassay was also conducted using sediment from the
station located north of the Port of Olympia peninsula.
Sample collection methods for the Olympia Yacht Club sample deviated
from the preferred practice in Puget Sound. The PSEP protocols (Tetra Tech
1986a) recommend the collection of 2 cm of surface sediments for sediment
chemistry and bioassay analyses. The Olympia Yacht Club sample was com-
posited from a 4-ft vertical core, which integrates a much longer period of
potential contaminant accumulation time than does the 2-cm sample. Because
additional data generated from samples collected from the surface 2 cm of
sediment are not available, the Olympia Yacht Club samples will be included
in this analysis.
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Data Synthesis--
Recent sediment bioassay data are synthesized below for analysis of EAR
values. State reasons for omitting effluent and receiving water bioassays
and focus on sediment bioassays.
Choice of Indicators—Because of the frequent use of the amphipod and
oyster bioassays and the existence of standardized techniques for both
(Chapman and Morgan 1983; Swartz et al. 1985), these assays were selected as
indicators of sediment toxicity. An extensive discussion comparing data
generated with amphipod and oyster larvae bioassays is provided in Tetra
Tech (1985b).
Available Data and Station Locations--The available amphipod bioassay
data were reviewed to determine whether the bioassays had been conducted on
previously frozen sediments, or whether a minimum of four replicates had
been conducted. Data from Everett Harbor suggest that toxicity is altered
by freezing the sediments (Tetra Tech 1985c). Because the ability of the
amphipod bioassay to distinguish differences in survival between control and
treatment sediments is dependent on the number of replicates and on the
number of individuals per replicate (see Table 1 in Swartz et al. 1985),
only those studies with a minimum of four replicates and 20 amphipods per
replicate were accepted. Based on the above criteria, data generated for the
U.S Army COE [no date (c)]f and data collected off the Port of Olympia
peninsula (Schiewe, M., 19 November 1987, personal communication) were
accepted. Each of these data sets was from one station.
Only one study used oyster larvae bioassays. Mr. M. Schiewe (19
November 1987, personal communication) conducted one replicated oyster larvae
bioassay on sediments collected off the Port of Olympia peninsula. Quality
control was adequate and the data were accepted.
To fully characterize sediment toxicity in Budd Inlet, additional data
are required from East and West Bays, the area north of the Port of Olympia
peninsula, and in the remainder of the inlet.
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Reference Area Data—Sediments used as native sand controls in the
accepted amphipod studies were used as reference sediments. Mr. M. Schiewe
(19 November 1987, personal communication) used sediment from Bowman's Bay as
reference material, while the U.S. Army COE [no date (c)] used sediment from
the amphipod collection site off West Beach, Whidbey Island as reference
material. Mean survival off the Port of Olympia peninsula was 99 percent
and mean survival at the Port of Olympia Yacht Club was 100 percent. The
oyster larvae bioassay reference was a seawater control. Mean oyster larvae
abnormality in seawater was 2 percent and mean mortality in seawater was 0
percent.
Elevation Above Reference (EAR) Analysis—Within each study, mortality
or abnormality (as appropriate) was compared between test and reference
conditions using appropriate statistical methods. Test sediment means for
each station were divided by the reference mean to yield the EAR. This
ratio indicates the relative magnitude of sediment toxicity. Results of
these analyses are provided in Table 14.
EAR values for amphipod and oyster mortality at the station off Cascade
Pole Company were 20 and 15, respectively. These EAR values are significant-
ly elevated according to the criteria established for the Everett Harbor
Action Plan (Tetra Tech 1985c). The mean reference mortality rate for the
amphipod bioassay off the Cascade Pole Company site was 1 percent, which
was comparable to the mean reference in Everett Harbor (Tetra Tech 1985c).
The mean oyster larvae mortality reference value was also 1 percent. This
value is 0.6 percent lower than the mean reference value obtained in Everett
Harbor (Tetra Tech 1985c).
The mean EAR for amphipod bioassays at the Olympia Yacht Club was 4.5.
This value was obtained using an amphipod control mortality rate of 1
percent. Sediment toxicity at the Olympia Yacht Club was not significant
according to the criteria established for the Everett Harbor Action Plan
(Tetra Tech 1985c).
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TABLE 14. SUMMARY OF EAR VALUES FOR AMPHIPOD
AND OYSTER LARVAE SEDIMENT BIOASSAYS
Study
Station
Mean Amphipod Amphipod Mean Oyster Oyster
Mortality (%) EAR Mortality (%) EAR
Scheiwe North of Port of
(19 November 1987)b Olympia peninsula
20
20a
15
15a
U.S. Army COE
[no date(c)]
Olympia Yacht Club
composite 1/2
Olympia Yacht Club
composite 3/4
6
3
6C
3C
a EAR calculation based on amphipod control mortality rate of 1.0 percent and oyster
control mortality rate of 1.0 percent.
b Personal communication.
c Mortality rate for amphipod control was 0.0 percent, however, to permit calculation
of EARs, a mortality rate of 1.0 percent was used.
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The lack of bioassay data for the remainder of Budd Inlet precludes a
comprehensive understanding of possible sediment toxicity. The data
presented in Table 14 should be considered preliminary, and conclusions
regarding sediment toxicity should be delayed until further data are
collected.
Benthic Infaunal Communities
Acceptable data that describe benthic communities in Budd Inlet are
lacking. A single study (Evergreen State College 1974) was conducted in
1974 at 37 stations located in upper Budd Inlet. However, sample collection
and laboratory analytical procedures were inconsistent with accepted PSEP
protocols. A review of these data suggests that a relatively diverse
assemblage of benthic infauna exists within the study area. However, the
data are inadequate to examine spatial gradients, and define and interpret
benthic communities.
Reliable benthic infauna data, including species richness and total
abundances, must be generated prior to the analysis of benthic infaunal
communities in Budd Inlet. Any sampling effort should provide adequate
spatial coverage, including the location of stations in West Bay, East Bay,
along the entrance channel, and in outer Budd Inlet.
Fish Pathology
Fish pathology data in Budd Inlet are lacking for the period 1982-1987.
The only available data were generated from samples collected by Malins et
al. (1980) in the winter, spring, summer, and fall of 1979. Data on liver
lesions and other pathological diseases in bottomfish, crabs, and shrimp
were collected and analyzed.
Most types of abnormalities were not observed in English sole, rock
sole, crabs, or shrimp captured in Budd Inlet. However, gill respiratory
epithelial hyperplasia was observed in 13 percent of the English sole, which
is a lower frequency than that observed in English sole from Hylebos
Waterway and Browns Point. Also, hepatocellular necrosis was observed in 11
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percent of the rock sole (ranked third behind the frequency of disease in
rock sole from Duwamish River and Case Inlet) and in 6 percent of the
English sole (ranked first with frequency of disease in English sole from
Hylebos Waterway, Case Inlet, and outer Elliott Bay). Because the raw data
were not available, the incidence of individual disorders cannot be linked
to particular stations. Summary information for English sole, rock sole,
and Pacific tomcod showed similar prevalences of abnormalities at Priest
Point (9.5 percent) and Olympia Shoals (13 percent). Data for samples
collected in West Bay were not presented independently. Higher incidences
of abnormalities were observed in crabs.
Although the cause of abnormalities in field-captured specimens has not
been determined, morphologically similar abnormalities have been induced in
laboratory mammals and fishes following exposure to carcinogens (Malins et
al. 1984). Thus, it is possible that the presence of such abnormalities in
organisms inhabiting Budd Inlet represents the effects of toxic substances
with carcinogenic characteristics.
Additional data are needed to provide a statistically valid interpre-
tation of histopathological abnormalities in bottomfish inhabiting Budd
Inlet. Bottom fish should be analyzed from East and West Bays, and the
central and northern portions of the inlet.
Fish Kills--
Prior to 1981, two fish kills were reported in Budd Inlet. Anaerobic
waters that entered Budd Inlet from Capitol Lake were determined to have
caused fish mortalities, and a fish kill occurred in the Deschutes River
near the Olympia Brewery (Kittle, L., 29 January 1988, personal communica-
tion). The most recent documented fish kill in Budd Inlet occurred in
September 1981 near the 4th Avenue and 5th Avenue Bridges in downtown
Olympia (Kittle, L., and H. Tracy, 19 January 1982, personal communication).
A discharge of anaerobic saltwater, which contained high concentrations of
hydrogen sulfide, entered Budd Inlet from Capitol Lake. The total estimate
of fish mortality was 314,098 non-salmonid fish and 100 salmonid fish of
which 50 were adults. Since that occurrence, no fish kills have been
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reported in Budd Inlet (Kittle, L., 29 January 1988, personal communication;
Singleton, L., 29 January 1988, personal communication). However, Mr. L.
Kittle noted that when Capitol Lake is lowered by the Washington Department
of Fisheries to release salmon fingerlings, mortalities may occur as
freshwater fish species enter the marine environment.
The formation of the anaerobic water in Capitol Lake that entered Budd
Inlet and caused massive fish mortalities was discussed in a memorandum
(Schmitten, R., 16 October 1981, personal communication) to Governor J.
Spellman:
"According to Ecology's findings, a deep hole has recently been
formed inside the lake [south of the gate] caused by backflushing
the lake with salt water from Budd Inlet for a variety of
operations. It is sometimes necessary and desirable to flush the
lake with salt water for fish releases, scrap fish control and
weed control in the spring. Under normal conditions the salt
water is replaced by Deschutes River water and the lake is
operated as a freshwater body for fish rearing and recreation.
However, in the fall when Deschutes River flows are naturally low,
any salt water entering the lake on extreme high tide through the
fish ladder or small leaks at the dam sinks to the bottom in the
deep hole and under certain conditions can stagnate. This
stagnant water which forms toxic hydrogen sulfide was the primary
cause of the September, 1981 fish kills in Budd Inlet."
The Washington Department of General Administration (WDGA), which
manages Capitol Lake, determined that it would not be plausible to fill in
the hole. Entrance Engineers (1983) completed an historical data review and
recommended appropriate actions to remedy the problem. In early 1987, a 12-
in diameter line was installed which operates as a siphon between Capitol
Lake and Budd Inlet. The intake for the siphon is located at a depth of 40
ft in the hole in Capitol Lake, and the siphon discharges directly north of
the tidal gate at a depth of 27 ft in Budd Inlet. Although the siphon can
be turned off, it is currently operating at all times and thus constantly
drains waters from within the area of the hole (Helmlinger, J., 23 March
1988, personal communication). The flow of water through the pipe is not
known (Sweet, B. 13 April 1988, personal communication). The WDGA currently
monitors waters from the area of the Capitol Lake hole from July to October
(Helmlinger, J., 13 April 1988, personal communication). Six water samples
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are collected at 2-m intervals from the surface to the bottom of the hole
and analyzed for dissolved oxygen, the frequency of sampling is dependent
on tide levels, algal blooms, and weather, at a minimum monitoring occurs 2
times/mo. According to Mr. Butch Sweet (23 March 1988, personal communica-
tion), the siphon appears to be working because the levels of dissolved
oxygen have never exceeded the limits established by Ecology (i.e., 2 mg/L).
These dissolved oxygen data have not been summarized but are available in a
daily field notebook from WDGA.
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IDENTIFICATION OF PROBLEM AREAS
The identification of problem areas is limited by the amount of
available data for Budd Inlet. Large gaps in data coverage exist for
eutrophication and toxic contamination, and an understanding of temporal
variability of microbial concentrations is lacking. Data gaps for these
categories will be discussed in the following section. Known problem areas
based on the available data are identified in this section.
Problem areas are ranked in this report at a level that is more general
than the numerical ranking in the decision-making approach. Therefore, if
additional data are collected, the results of the ranking presented in this
report should be re-evaluated by implementing the decision-making approach.
Criteria are established to define problem areas, and three levels of
problem severity are defined within each category: highest priority,
secondary priority, and no immediate action. Highest priority problem areas
are recommended for further source and remedial action evaluation. Secon-
dary priority problem areas should be thoroughly studied to define the
extent and severity of the problem. Areas designated for no immediate
action are recommended for future monitoring.
EUTROPHICATION
Nutrient and dissolved oxygen concentrations were discussed in the "Data
Summaries" section for eutrophication. Elevated or depressed nutrient
concentrations are not environmental problems by themselves. However,
elevated nutrient concentrations may provide the essential ingredients for
algal blooms that contribute to dissolved oxygen depletion in Budd Inlet.
Low oxygen concentration is an environmental problem because resident fish
and invertebrates cannot support normal metabolic activities when oxygen
levels decline. The amount of oxygen required to support normal metabolic
rates varies among species. However, oxygen concentrations less than 3.0
mg/L are considered detrimental to both fish and invertebrates (Welsh, B.(
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18 November 1987, personal communication). The highest priority problem
areas for eutrophication are defined as those areas experiencing less than
3.0 mg/L dissolved oxygen at least once during the period 1982-1987 (Table
15). Secondary priority problem areas are defined as having dissolved
oxygen concentrations of 3.0-5.0 mg/L during the same period. The Class B
water quality standard of 5.0 mg/L was used as the upper limit for the
secondary priority designation. Areas where oxygen levels remain above 5.0
mg/L throughout the year are not problem areas and require no immediate
action. Class A water quality criteria (i.e., 7 mg/L) should be the desired
endpoint of water quality remediation programs.
The highest priority problem areas for eutrophication were Ecology
Station BUD002 in West Bay, the City of Olympia station at the Capitol Lake
outfall to Budd Inlet, and the Port of Olympia stations in the East Bay
Marina (see Table 3). Dissolved oxygen concentrations in late summer were
less than 3.0 mg/L at the bottom of the water column at these stations.
Secondary priority areas were City of Olympia stations at the Fiddlehead
Marina, north of the LOTT 30-in diameter outfall, and in the navigation
channel northeast of Cascade Pole Company. No problem areas were identified
north of East and West Bays, but there was only one sampling station where
dissolved oxygen was monitored (i.e., Ecology Station BUD005 just south of
Olympia Shoals).
MICROBIAL CONTAMINATION
Identification of microbial contamination problem areas is based on
departures from the Washington State water quality standards described in
the microbial contamination section of "Data Summaries." The fecal coliform
bacteria EAR values were derived from calculations of geometric means within
each portion of Budd Inlet depicted in Figure 16. EAR values for areas
within Class A waters were calculated using the Class A water quality
criteria of 14 organisms/100 mL as reference. EAR values for areas within
Class B waters incorporated the Class B water quality criteria of 100
organisms/100 mL.
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TABLE 15. LIST OF PRIMARY AND SECONDARY
PROBLEM AREAS IN BUDD INLET3
Primary
Secondary
Eutrophication
Toxic Contamination
Sediment Chemistry
Microbial Contamination
Ecology Station BUD002
Capitol Lake outfall
to Budd Inlet
East Bay Marina
Cascade Pole Co.
West Bay drain
Moxlie Creek
Boston Harbor
Ellis Creek
South of Tykle Cove
Fiddlehead Marina
North of LOTT 30-in outfall
Northeast of Cascade Pole Co.
middle of channel
West Bay, near the West Bay
drain
Fiddlehead Marina
Tamoshan
Beverly Beach
Athens Beach
Butler Cove
North of Priest Point
a Criteria for prioritizing problem areas are found in Table 3, and are
discussed in the text.
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The criteria for identifying problem areas were based on the logarithmic
scale. Fecal coliform bacteria EAR values in the highest priority areas
exceeded 10. Secondary priority areas for fecal coliform bacteria had EAR
values between 1 and 10. Areas with fecal coliform bacteria EAR values
below 1 were not considered for immediate action.
The highest priority problem areas for fecal coliform bacteria in Budd
Inlet were Moxlie Creek, Boston Harbor, Ellis Creek, and a creek entering
Budd Inlet south of Tykle Cove. Secondary priority problem areas included
Tamoshan WWTP, Beverly Beach WWTP, Athens Beach, Butler Cove, and north of
Priest Point. The variability inherent in the bacterial counts at stations
sampled more than once suggests that routine sampling at these stations is
essential to better assess the spatial extent and magnitude of the problem
areas. Fecal coliform bacteria samples have not been collected at all
potential sources. Point sources of microbial contamination to Budd Inlet
that have not been adequately characterized, include the Tamoshan, Beverly
Beach, and Seashore Villa WWTP. Nonpoint sources that have not been
characterized include the contribution of microbial contamination from
failing septic systems, local hobby farms, live-aboards in Olympia marinas,
and general boating activities in Budd Inlet.
TOXIC CONTAMINATION
The following six data categories were discussed in the "Data Summaries"
section for toxic contamination: water column contamination, sediment
contamination, bioaccumulation, bioassay results, benthic communities, and
fish pathology. The following discussion of toxic problem areas will be
limited to sediment chemistry and bioassay results. Bioaccumulation of clam
tissues is not included because of the high detection limits of the reference
data. Water column contamination, benthic communities, and fish pathology
are not included because of a lack of data or a lack of Budd Inlet reference
criteria.
Because the lack of data precluded following the guidelines set forth
in the decision-making approach, the criteria for sediment chemistry and
bioassays are derived from the Everett Harbor Action Plan (Tetra Tech
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1985c). The highest priority problem areas for sediment chemistry in Budd
Inlet are defined as those stations where the EAR values for metals exceeds
50, or where the EAR for organic compounds exceeds 100 (see Table 3).
These values correspond to the maximum EAR categories in the Everett Harbor
Action Plan (Tetra Tech 1985c). Secondary priority problem areas are
defined as areas where the EAR for sediment metals is between 10 and 50, or
where the EAR for organic compounds is between 10 and 100. No immediate
action areas are those with EAR values below 10.
The highest priority sediment chemistry problem areas in Budd Inlet are
near the Cascade Pole Company site and at the West Bay storm drain. These
are the only locations where sediment chemical analyses for organic compounds
were conducted. Additional sampling and analysis is required to fully
describe the geographic extent of contamination in these areas. Secondary
priority problem areas were located in West Bay off of the West Bay storm
drain (sediment organic compounds), and in the Fiddlehead Marina (sediment
metals). Sediment metals were investigated at the Capitol Lake outfall but
were found at levels that required no immediate action. The remainder of
Budd Inlet has not been investigated for sediment contamination.
Problem areas for sediment bioassay results were defined based on
percent mortality instead of the EAR value because the EAR value is greatly
influenced by percent mortality in the control bioassay test. For example,
if the mortality in the test sediment was 25 percent, the EAR based on a 1
percent control mortality would be 25. The EAR based on a 3 percent
control mortality would be 8.3. Conclusions drawn from these two EAR values
could be very different. Only those data having less than 5 percent
mortality in the control test were accepted for this review.
Highest priority problem areas are defined as those areas where either
the amphipod bioassay or the oyster bioassay resulted in greater than 50
percent mortality (see Table 3). This mortality corresponds to the maximum
value EAR in the Everett Harbor and the Elliott Bay Action Plans (Tetra Tech
1985b,c). Secondary priority problem areas occur where either of the
bioassay mortality rates were between 25 and 50 percent. Stations with less
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than 25 percent mortality for either of the bioassays requires no immediate
action.
Bioassays were conducted at only two stations in Budd Inlet. Neither
the station off the Port of Olympia peninsula nor the station at the Olympia
Yacht Club require immediate action.
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IDENTIFICATION OF DATA GAPS
Intensive synoptic sampling programs have not been conducted in Budd
Inlet. As discussed in "Identification of Problem Areas," this lack of
synoptic data has greatly hindered the identification of problem areas. All
appropriate data were used to identify problem areas caused by eutrophi-
cation, toxic contamination, and microbial contamination. More complete
characterization of Budd Inlet will require the collection and analysis of
additional data. The objective of this final section is to identify data
gaps that, when filled, will enable full use of the decision-making approach
to characterize environmental conditions in Budd Inlet.
The following discussion provides information that may be used to
design a preliminary field investigation. A detailed sampling and analysis
plan for development of the Budd Inlet Action Program will be prepared at a
future date.
EUTROPHICATION
The problem of eutrophication in upper Budd Inlet has been well
documented (URS 1986). However, the boundaries of the geographic area
impacted by high nutrient levels and low dissolved oxygen have not been
delineated. Existing data were collected to monitor specific areas (i.e.,
Fiddlehead Marina, Capitol Lake outfall, East Bay Marina). Additional
sampling efforts should be conducted south of Priest Point to generate data
that could define the spatial extent of problem areas in southern Budd
Inlet. Stations located north of Priest Point would provide reference
conditions.
Information on dissolved oxygen and nutrients should be collected to
fill gaps in the available eutrophication data because both types of
measurements are necessary to define the spatial extent and magnitude of the
eutrophication problem. A detailed dissolved oxygen data collection effort
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coupled with a smaller nutrient data collection effort at overlapping
stations would be a cost-effective method for obtaining the necessary infor-
mation. Detailed information on dissolved oxygen concentrations is most
important because of the deleterious effects of low dissolved oxygen on the
resident biota. Oxygen measurements at each station should occur at the
sediment surface and in the water column to provide information on the
oxygen levels to which the plankton, nekton, benthic epifauna, and benthic
infauna are subjected. Additionally, nonpoint sources of nitrogen (including
atmospheric deposition) should be quantified.
Oxygen depletion is a seasonal phenomenon. Lowest oxygen levels occur
in late summer and early fall in the bottom water. An intensive weekly
sampling effort from July through September would provide the necessary
information to understand this annual event. Sampling stations should
overlap with existing monitoring stations. Information collected at the
existing monitoring stations between October and June would provide the
necessary data for the remainder of the year.
MICROBIAL CONTAMINATION
Considerable data exists for fecal coliform bacteria contamination in
Budd Inlet. Data collected from shoreline sources were generally higher in
September 1985 than in April 1985 (URS 1986). The cause of this variability
may have been differences in the flow rates of the freshwater sources that
were sampled. It was suggested that higher flow rates may correspond to
increased fecal coliform bacteria concentrations (URS 1986).
Information from offshore monitoring stations indicated that fecal
coliform concentrations in offshore surface waters were within Washington
State standards between 1982 and 1986. Continuation of these programs will
be sufficient to help understand fecal coliform bacterial distributions in
offshore areas.
Routine data collection for fecal coliform bacteria and water flow at
selected locations would help define the relationship between these vari-
ables. Sampling locations might include sites receiving storm water
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discharges from urban areas and sites receiving discharges from rural areas.
Moxlie Creek should be sampled for the purpose of monitoring urban runoff
since it is an identified problem area for microbial contamination. Moxlie
Creek enters East Bay via an 84-in diameter pipe and enters the pipe near
Plum and Union Streets in Olympia. Approximately 100 ft before the outfall
terminus, the East Bay CSO discharges into Moxlie Creek (see the section
entitled "Contamination Sources"). Sites such as Ellis Creek or the creek
entering Budd Inlet between Tykle Cove and Butler Cove might be suitable for
monitoring rural runoff. Both of these sites are also known problem areas.
Fecal coliform bacteria monitoring in marine waters should also occur
near the Tamoshan, Beverly Beach, and Seashore Villa WWTP- Monitoring
stations located in streams or culverts and in marine waters near Athens
Beach and the French Hill Road would also be appropriate.
TOXIC CONTAMINATION
Sources of Contamination
The limited sediment chemistry data presently available for Budd Inlet
clearly indicated that the upper inlet is receiving contaminated material
from the Port of Olympia peninsula. The only point source of contamination
that has been sampled is the West Bay storm drain. According to Mr. R. Alan
(25 March 1988, personal communication), LOTT has not conducted any sampling
off the CSOs. Other sources, including NPDES-permitted discharges, storm
drains carrying storm runoff from urban areas, and seeps and groundwater at
the Cascade Pole Company site should also be investigated. This information
is required to identify contaminant sources for remedial action.
Sediment Chemistry
At the present time, Budd Inlet sediments have not been analyzed for
all of the Budd Inlet contaminants of concern (see Table 2). Analyses of
sediments near the Cascade Pole Company have been limited to organic
chemicals present in creosote and the suspected breakdown products of
creosote. Analyses of sediment metals are limited to three City of Olympia
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stations, and seven stations near the Cascade Pole Company. The full suite
of metals of concern were not investigated at these stations.
A sampling program was proposed by Tetra Tech (1987) for sediments near
the Cascade Pole Company. If this plan is implemented, the chemical results
will adequately describe sediment contamination in the immediate area.
However, sampling efforts in East Bay are needed to document the geographic
extent of organic contamination from the Cascade Pole Company. This
sampling would also indicate whether sediments have been contaminated by
Moxlie Creek, by any of the East Bay storm drains, or by the East Bay
Marina.
Sampling in West Bay is needed to gather data to determine potential
sediment contamination from storm drains, CSOs, the LOTT 48-in diameter
outfall at Fiddlehead Marina, and from other industrial discharges and
marinas. Sediment chemistry information from sampling north of the Port of
Olympia peninsula will provide information on the geographic extent of
sediment contamination north of the industrial portions of Budd Inlet.
Sediment chemistry information from near Gull Harbor is needed to
determine whether environmental degradation resulted from the extended
anchorage of the Mothball Fleet. This maritime fleet contained over 100
vessels between the end of World War II and the early to mid 1960s (Jamison,
D., 21 January 1988, personal communication; Newall, G., 10 February 1988,
personal communication). Solvents, waste oils, and unknown objects were
reportedly dumped into the inlet from the ships and shore-based facilities.
Bioaccumulation
The bioaccumulation of organic contaminants in Budd Inlet clams was
investigated near the Cascade Pole Company and the West Bay storm drain. No
additional data are available for the study period. The majority of the
bioaccumulation data from other urban embayments in Puget Sound are for
English sole muscle and liver tissues. Information on bioaccumulation of
organic compounds and metals in English sole is needed to determine the
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bioavailability of contaminants in Budd Inlet, and to enable comparisons
between conditions in Budd Inlet and conditions in other urban bays.
Collection of English sole for bioaccumulation analysis should occur in
East and West Bays, near the Port of Olympia peninsula, near Priest Point,
near Gull Harbor, and in areas of Budd Inlet that could provide reference
data. The information collected would enable differences between East and
West Bays to be defined, and would provide information on the geographic
extent of bioaccumulation north of the industrialized portions of the inlet.
The sampling area near Gull Harbor would provide information on bioavai1-
ability of sediment contaminants that may have come from the Mothball Fleet.
Sediment Toxicity
Sediment toxicity was investigated north of the Port of Olympia
peninsula and at the Olympia Yacht Club. No toxicity data are available for
the sediments near the Cascade Pole Company that are known to be highly
contaminated with organic chemicals. Similarly, no toxicity data are
available for sediments near NPDES-permitted discharges, CSOs, and storm
drains.
Bioassay tests of sediments collected near known and suspected contam-
inant sources would provide important information about the magnitude of
environmental degradation at those locations. Bioassay tests are needed for
sediments in East and West Bays, north of the Port of Olympia peninsula, near
Priest Point, and near Gull Harbor. Tests using both amphipods and oyster
larvae would enable comparisons to be made with toxicity information from
other Puget Sound urban bays. Microtox tests might also be considered to
determine the relative toxicity of sediment contaminants to bacteria.
Benthic Infaunal Communities
As mentioned in the "Data Summaries" section, there are no acceptable
data concerning benthic infaunal communities in Budd Inlet. A solid
understanding of the composition of the benthic community in Budd Inlet is
important for determining the effects of sediment contaminants and the
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effects of low dissolved oxygen on the resident biota. The selection of
sampling locations for benthic community analyses must be carefully con-
sidered. Stations where sediments are known to be contaminated (determined
by sediment chemistry analyses), and stations where sediments are known to be
influenced by low dissolved oxygen (determined by water quality surveys) must
be sampled. Stations should exhibit similar grain size distributions, and
should be located at similar depths so that resulting data may be compared.
Under these conditions, the individual effects of sediment contamination and
low dissolved oxygen concentrations may be determined.
A series of stations north of the Port of Olympia should be sufficient
to identify the extent of benthic degradation to the north. Selection of
appropriate reference stations is very important because reference conditions
for benthic infauna in Budd Inlet may differ from reference conditions
established in other parts of Puget Sound. Reference data from areas such
as Carr Inlet (Tetra Tech 1985a) may not be appropriate for comparison with
data from Budd Inlet.
Fish Histopatholoqy
Available data for fish histopathology in Budd Inlet are lacking for
the study period 1982-1987. Earlier data collected by Mai ins et al. (1980)
indicated that the incidence of certain pathological lesions in English sole
and rock sole was similar to the incidence of these lesions in other urban
bays. A data collection effort is needed to determine the incidence of
bottomfish histopathological disorders in Budd Inlet. English sole should
be used in the collection effort so that data on histopathology in Budd
Inlet may be compared with data on histopathology in other Puget Sound urban
bays.
Histopathological data should be generated at the same areas as were
described for bioaccumulation studies. Data would therefore be collected
from areas suspected to have elevated sediment contaminants, and from
reference areas that are not suspected to be contaminated.
132
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OTHER DATA GAPS
Data on motile epifauna and bottomfish are also necessary to fully
define the effects of eutrophication and oxygen depletion. Considerable
data on the impact of oxygen depletion on fish distributions (Johnson, M.,
18 November 1987, personal communication) are now being collected on the
Atlantic coast in Long Island Sound. These data demonstrate that as oxygen
concentration declines, motile epifauna and bottomfish move out of the
affected area possibly seeking water containing higher oxygen concentra-
tions. Bottom trawl sampling could help determine the composition of the
fish community in relation to dissolved oxygen concentration, and would
provide valuable information on the effects of oxygen depletion. Weekly or
semi-monthly trawls in East and West Bays, and in one or two reference areas
would provide information to determine whether oxygen depletion was impacting
the motile fauna in Budd Inlet.
133
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Engineers, Regulatory Functions Branch, Seattle, WA. 1 pp.
U.S. Environmental Protection Agency. 7 January 1988. Personal Communica-
tion (unpublished data from STORE!). U.S. EPA Region X, Seattle, WA.
URS. 1980. State of Washington industrial waste survey, City of Olympia.
Prepared for Washington Department of Ecology, Olympia, WA. URS Company,
Seattle, WA. 32 pp. + appendices.
URS. 1986. Southern Puget Sound water quality assessment study. Final
report: comprehensive circulation and water quality study of Budd Inlet.
Prepared for Washington Department of Ecology, Olympia, WA. URS Corporation,
Seattle, WA. 222 pp. + references and appendices.
Washington Department of Ecology. 1979. National pollutant discharge
elimination system waste discharge permit. Seashore Villa Mobile Home Park.
Permit No. WA-003727-3. Washington Department of Ecology, Olympia, WA.
9 pp.
Washington Department of Ecology. 1980. National pollutant discharge
elimination system waste discharge permit. Beverly Beach Utilities Associa-
tion. Permit No. WA-003806-7. Effective date 16 September 1980. Washington
Department of Ecology, Olympia, WA. 10 pp.
Washington Department of Ecology. 1984. Potential hazardous waste site
preliminary assessment: Water Street pump station. Site identification No.
WA D980835144. Washington Department of Ecology, Olympia, WA. 6 pp.
Washington Department of Ecology. 1985a. National pollutant discharge
elimination system waste discharge permit. Chevron U.S.A., Inc. Permit No.
WA-003871-7. Effective date 25 June 1985. Washington Department of
Ecology, Olympia, WA. 10 pp.
144
-------
Washington Department of Ecology. 1985b. National pollutant discharge
elimination system waste discharge permit. Delson Lumber, Inc./DWS Inter-
national, Inc., and Olympia Forest Products Company. Permit No. WA-002154-
7. Effective date 16 December 1985. Washington Department of Ecology,
Olympia, WA. 12 pp.
Washington Department of Ecology. 1986. National pollutant discharge
elimination system waste discharge permit. Thurston County Public Works,
Tamoshan Development. Permit No. WA-003729-0. Effective date 20 October
1986. Washington Department of Ecology, Olympia, WA. 14 pp.
Washington Department of Ecology. 1987. National pollutant discharge
elimination system waste discharge permit. Cities of Tumwater and Lacey,
Thurston County, and the City of Olympia. Permit No. WA-003706-1. Effective
date 25 September 1987. Washington Department of Ecology, Olympia, WA. 21
pp.
Washington Department of Ecology. 9 December 1987. Personal Communication
(information to Ms. Karen L. Keeley; computer data listing from Washington
Department of Ecology for reported spills and complaints regarding Budd
Inlet, September 1986 to November 1987). Washington Department of Ecology,
Olympia, WA. 1 p.
Washington Department of Fisheries. 1979. Marine water quality compendium
for Washington State. Volume II Data. Grant No. R805032010. Prepared for
U.S. Environmental Protection Agency, Environmental Research Laboratory,
Corvallis, OR. Washington Department of Fisheries, Research and Development
Division, Olympia, WA. 528 pp.
Welsh, B. 18 November 1987. Personal Communication (information to Ms.
Betsy Day; causes and effects of oxygen depletion in Long Island Sound).
Long Island Sound Hypoxia-Modeling Workshop, University of Connecticut,
Groton, CT.
Westley, R.E., E. Finn, M.E. Carr, M.A. Tarr, A.J. Scholz, L. Goodwin, R.W.
Sternberg, and E.E. Collins. 1975. Evaluation of effects of channel
maintenance dredging and disposal on the marine environment in southern
Puget Sound, Washington. Washington State Department of Fisheries, Olympia,
WA. 308 pp.
White, M. 30 July 1987. Personal Communication (memorandum to Cascade Pole
Company file; field notes from sampling of product seeps and survey of wells
for product on 24 June 1987). Washington Department of Ecology, Olympia, WA.
White, M. 21 January 1988. Personal Communication (information to Ms.
Karen L. Keeley; intertidal seps from Cascade Pole Company). Washington
Department of Ecology, Olympia, WA.
Yake, B. 6 July 1981. Personal Communication (memorandum to Mr. John
Bernhardt, Washington Department of Ecology; interpretation of June 3, 1981
Budd Inlet data with particular respect to oxygen depletion). Washington
Department of Ecology, Olympia, WA.
145
-------
Yake, B., J. Joy, and A. Johnson. 1984. Chemical contaminants in clams and
crabs from Eagle Harbor, Washington State, with empahsis on polynuclear
aromatic hydrocarbons. Segment No. 25-00-01. Washington Department of
Ecology, Olympia, WA.
146
-------
APPENDIX A
DATA EVALUATION SUMMARY TABLES
-------
APPENDIX A: DATA EVALUATION SUMMARY TABLES
Data evaluations are summarized for water quality, contaminant sources,
sediment contamination, bioaccumulation, and sediment toxicity in Appendix
A. Two summaries are provided for each type of data. The first table
(Tables A-l, 2, 3, 4) lists evaluation summaries for documents reviewed for
Budd Inlet during the 1982-1987 study period. The adequacy of procedures
for sample collection, sample handling, quality assurance, and analytical
methods are evaluated. Analytical methods refers to statistical analyses in
biological studies and to laboratory analytical techniques in all other
studies. The decision to accept or reject each study is based on adequacy
of the procedures. Full references for each study can be found in the Budd
Inlet bibliography (Appendix E).
The second table (Tables A-5, 6, 7, 8) provides a summary of data
within the accepted studies. Each summary includes author/year citation,
period of study; type of samples collected, variables measured or analyzed,
number of stations, number of replicates per station, and number of times a
station was sampled during the study period.
A-l
-------
TABLE A-l. DATA EVALUATION SUMMARY FOR WATER QUALITY STUDIES3-5
Reference Acceptable
Alan (24 September 1987)c
Armstrong (17 November 1987) c
Bernhardt and Yake (22 June 1983) c
Egge (25 January 1987)c
Kendra and Determan
(6 November 1985) c
Kessler (18 December 1987)c
Mumford (25 September 1987) c
Pierce (22 October 1987) c
Pierce (22 October 1987)c
R.W. Beck and Associates (1986)
Thurston County Health Department
(1985)
URS (1986)
Yes
Yes
No
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
SC
A
N
A
A
A
N
N
N
N
A
A
SH
N
N
N
N
N
N
N
N
N
A
A
QA
N
N
N
N
N
N
N
N
N
N
N
AM
A
N
A
A
A
N
N
N
A
A
A
Comments
LOTT WWTP
Priest Point
Review of data before LOTT
became a secondary WWTP
East Bay Marina
Tamoshan, Beverly Beach, and
Seashore Villa WWTPs
Provides methods for Alan
(24 September 1987a)c
WDNR Marine Station
Fecal col i form bacteria -
Budd Inlet
Fecal col i form bacteria -
Olympia Marina
Fecal col i form bacteria -
Boston Harbor
Fecal col i form bacteria -
Budd Inlet
Fecal col i form bacteria -
Budd Inlet
a Refer to summary of accepted water quality studies (Table A-5) for variables
measured.
k A = adequate, N = not available, SC = sample collection, SH = sample handling,
QA = quality assurance/quality control, AM = analytical methods.
c Personal communication.
A-2
-------
TABLE A-2. DATA EVALUATION SUMMARY FOR CONTAMINANT SOURCE STUDIES3-5
Reference
Acceptable SC SH QA AM DL
Comments
Applied Geotechnology Yes
(1986a,b)
Johnson (22 July 1985)° Yes
Norton (5 February 1986)c Yes
A A A A A
A/I N N N N
A A A/N A N
Soils, groundwater at
Cascade Pole Company
Storm drain, seep near
Cascade Pole Company
Storm drain, sediment near
Cascade Pole Company
a Refer to summary of accepted contaminant source studies (Table A-6) for variables
measured.
b A = adequate, I = inadequate, N = not available, SC = sample collection, SH = sample
handling, QA = quality assurance/quality control, AM = analytical methods, DL =
detection limits.
c Personal communication.
A-3
-------
TABLE A-3. DATA EVALUATION SUMMARY FOR SEDIMENT CONTAMINATION
AND BIOACCUMULATION STUDIES3'15
Reference Acceptable SC
Alan (24 September 1987)c-d
Applied Geotechnology (1987)
Calambokidis et al . (1984)
Calambokidis et al . (1985)
GeoEngineers (1987)
Johnson (22 July 1985)c
Norton (5 February 1986) c
Turpin and Associates (1985)
U.S. Army COE [no date (c)]
Yes
No
No
No
No
Yes
Yes
No
No
A
I
N
N
I
A/ 1
A
I
I
SH
N
A
N
N
A
N
A/ 1
N
N
QA
N
A
N
N
N
N
A
A
A
AM
A
A
A
A
A
N
A
A
N
DL
N
A
A
A
A
N
N
A
N
Comments
LOTT WWTP
Cascade
Southern
Southern
Port of
Cascade
Cascade
One Tree
Olympia
Pole Company
Puget Sound
Puget Sound
Olympia - Berth 3
Pole Company
Pole Company
Island Marina
Yacht Club
a Refer to summary of accepted sediment contamination and bioaccumulation studies
(Table A-7) for variables measured.
b A = adequate, I = inadequate, N = not available, SC = sample collection, SH = sample
handling, QA = quality assurance/quality control, AM = analytical methods, DL =
detection limits.
c Personal communication.
d Field and laboratory methods are presented in Kessler (18 December 1987, personal
communication).
A-4
-------
TABLE A-4. DATA EVALUATION SUMMARY FOR SEDIMENT TOXICITY STUDIES3
Reference Acceptable SC SH QA AM A/0 Comments
Schiewe (19 November 1987)b Yes A A A A A/0 North of Port
of Olympia
U.S. Army COE [no date (c)] Yes N N A A A Olympia Yacht Club
a A = adequate, I = inadequate, N = not available, SC = sample collection, SH = sample
handling, QA = quality assurance/quality control, AM = analytical methods, A/0 =
amphipod/oyster larvae bioassay.
b Personal communication.
A-5
-------
TABLE A-5. SUMMARY OF ACCEPTED WATER QUALITY STUDIES3
Reference
Alan (24 September 1987) b
Armstrong (17 November 1987 )b
Egge (25 January 1987)b
Kendra and Determan (6 November 1985 )b
Mumford (25 September 1987 )b
Pierce (22 October 1987 )b
j> Pierce (22 October 1987) b
i
°* R.W. Beck and Associates (1986)
Thurston County Health Department (1985)
URS (1986)
URS (1986)
URS (1986)
Sampl e
Type
we
Sh
we
we
we
Sh
we
we
we
we
we, so
we
Variables
Nu, FC, TSS,
BOD, pH, T, S, D
FC
T, C
Nu, FC, TSS,
pH, T, S, D
Nu, pH, T, S, D
FC
FC
FC
FC
FC
Nu, FC, BOD
T, S, D, CM
Survey Number of
Period Stations
1/15/86-
11/12/86
6/10/86-
6/22/87
7/9/85-
10/28/87
6/17/85-
7/2/85
12/1/81-
11/17/82
7/85-3/86
8/15/85
4/19/84
4/9,15,17/85
9/10,11/85
4/9,15,17/85,
9/10,11/85
9/84, 5/85
5
1
2
26
1
24
3
9
57
57
11
8
Number of
Repl icates
1
1
1
1
1
1
2
1
1
1
1
1
Number of
Times Sampled
Varied
5
Vari ed
1
44
1
1
1
1
1
2
2
Comments
LOTT WWTP
Priest Point
East Bay Marina
Tamoshan, Beverly Beach,
and Seashore Villa WWTPs
WDNR Marine Station
Budd Inlet
Port of Olympia Marina
Boston Harbor
Budd Inlet
Budd Inlet
Budd Inlet
Budd Inlet
a WC = water column, Sh = shellfish, SD = storm drain, Nu = nutrients, FC = fecal coliform bacteria, TSS = total suspended solids, BOD = 5-day biochemical oxygen
demand, T = temperature, S = salinity, D = dissolved oxygen, CM = current meter.
Personal communication.
-------
TABLE A-6. SUMMARY OF ACCEPTED CONTAMINANT SOURCE STUDIES3
Reference
Applied Geotechnology (1986a,b)
Johnson (22 July 1985)b
Norton (5 February 1986) b
White (30 July 1987)b
Sample
Type Variables
6, SW Org
Water, G Org, Conv
Water Org, Conv
Water, product Org
Survey
Period
7/85
2/13/85
8/14/85
6/24/87
Number of
Stations
Varied
3
1
5
Number of
Repl icates
Varied
1
1
0
Number of
Times Sampled
Varied
1
1
1
Comments
Cascade Pole Company outfall,
groundwater seep
Cascade Pole Company outfall.
West Bay drain, groundwater
seep
West Bay drain
Cascade Pole Company ground-
water and product seeps
a 6 = groundwater, SW = surface water, SD = storm drain, Org = organics, Conv = conventionals (e.g., grain size, total organic carbon).
Personal communication.
-------
TABLE A-7. SUMMARY OF ACCEPTED SEDIMENT CONTAMINATION AND BIOACCUMULATION STUDIES3
Reference
Alan (24 September 1987)b
Johnson (22 July 1985)b
Norton (5 February 1986} b
Sample
Type
Sed
Sed
Sed, B
Variables
Me, Nu, TS, TVS
Me, Org
Org, Conv
Survey
Period
4/23/86
2/13/85
8/14/85
Number of
Stations
3
8
7
Number of
Replicates
1
1
1
Number of
Times Sampled
1
1
1
Comments
LOTT WWTP
Cascade Pole Company
Cascade Pole Company
a Sed = sediment, B = bioaccumulation. Me = metals, Org = organics, Nu = nutrients, TS = total solids, TVS = total volatile solids, Conv = conventional (e.g., grain
size).
" Personal communication.
I
00
-------
TABLE A-8. SUMMARY OF ACCEPTED SEDIMENT TOXICITY STUDIES3
Reference
Sample
Type
Variables
Survey
Period
Number of
Stations
Number of
Replicates
Number of
Times Sampled
Comments
Schiewe (19 November 1987)b
U.S. Army COE [no date (c)]
Sed
Sed
0, A
3/85
NA
North of Port of Olympia
Peninsula
Olympia Yacht Club
Sed = sediment, 0 = oyster, A = amphipod, NA = not available.
Personal communication.
UD
-------
APPENDIX B
MONTHLY AVERAGES OF WATER QUALITY DATA AT ECOLOGY
AMBIENT MONITORING STATIONS BUD002 AND BUD005
-------
TABLE B-1. MONTHLY AVERAGES OF WATER QUALITY DATA COLLECTED
FROM 1982 TO 1986 AT ECOLOGY AMBIENT WATER QUALITY
MONITORING STATIONS BUD002 AND BUD005a
Station
BUD002
BUD005
Month
April
May
June
July
August
September
October
November
Apr i I
May
June
July
August
September
October
November
Surface
D0b
10.2/0.5
10.7/0.7
10.2/1.0
9.0/1.9
9.0/2.4
6.1/0.7
6.9/0.9
8.2/1.0
11.4/1.1
11.5/1.1
11.3/0.5
11.9/1.1
10.8/2.0
9.8/2.7
8.7/0.7
8.4/1.0
Bottom
DO
9.9/0.7
9.6/1.2
8.7/2.4
6.6/1.4
6.1/1.9
4.1/1.9
6.9/1.3
6.9/0.67
10.4/0.7
11.2/0.9
10.0/2.2
8.8/2.9
7.4/1.5
7.0/1.1
7.5/0.6
7.4/1.4
Surface
NH3+NH4"C
0.5/0.1
0.12/0.07
0.11/0.04
0.05/0.04
0.09/0.08
0.20/0.05
0.11/0.06
0.11/0.01
0.09/0.06
0.03/0.03
0.05/0.06
0.02/0.01
0.02/0.01
0.06/0.05
0.02/0.01
0.06/0.02
Bottom
NH3+NH4~
0.12/0.06
0.09/0.03
0.16/0.07
0.06/0.06
0.05/0.07
0.22/0.11
0.07/0.05
0.06/0.02
0.09/0.07
0.06/0.04
0.08/0.03
0.03/0.04
0.03/0.04
0.09/0.08
0.03/0.01
0.02/0.0
Surface
0-P04d
0.05/0.02
0.05/0.02
0.06/0.03
0.07/0.02
0.06/0.04
0.12/0.09
0.05/0.01
0.10/0.12
0.06/0.02
0.03/0.02
0.05/0.03
0.06/0.02
0.06/0.02
0.07/0.03
0.05/0.01
0.05/0.01
Bottom
0-P04
0.06/0.02
0.06/0.03
0.10/0.06
0.06/0.01
0.05/0.02
0.09/0.04
0.08/0.05
0.05/0.01
0.05/0.02
0.05/0.03
0.06/0.03
0.04/0.01
0.05/0.01
0.08/0.04
0.05/0.01
0.05/0.01
a Values expressed as mean/one standard deviation (mg/L).
DO dissolved oxygen.
c NH-j+NH4~ - nitrate plus ammonium.
0-P04 ortho-phosphate.
B-1
-------
APPENDIX C
HISTORY OF SEDIMENT DREDGING IN BUDD INLET
-------
APPENDIX C
HISTORY OF SEDIMENT DREDGING IN BUDD INLET
The most recent maintenance dredging of navigation channels in Budd
Inlet occurred in 1973 (Parker, B., 6 October 1987, personal communication).
At this time, Washington State evaluated the effects of channel maintenance
dredging and disposal of sediments on the marine environment (Westley, R.E.,
et al. 1975). A computerized list of all dredging permits issued by U.S.
Army COE since January 1975 in Budd Inlet, Capitol Lake, and the Deschutes
River was obtained. Since 1980, 11 permits have been issued. These permits
were reviewed and are summarized in Table D-l. In some cases, it was
determined that dredged materials were contaminated, and the locations of
these contaminated soils are plotted on Figure 5. If the contaminated
sediments are disposed offshore, the disposal process is managed by U.S.
Army COE. If the soils are deposited on an upland site, Ecology is respon-
sible for management.
In early 1988, the U.S. Army COE (Babcock, S., 6 October 1987, personal
communication) will publish a reconnaissance survey document entitled
"Olympia Harbor, Washington, Navigation Improvements." The purpose of this
document is to conduct a preliminary appraisal of a plan to modify the
deepwater Olympia channel that enters West Bay. Although this report will
not summarize environmental data, sediment testing may be required if the
channel is modified.
C-l
-------
TABLE C-1. LIST OF DREDGING PERMITS ISSUED FOR BUDD INLET SINCE 1980
Permittee3
Date
Permit I saucer*
Purpose
Reference
o
i
ro
City of Olympia
Fiddlehead Marina
Martin Marina
Olympia Yacht Club
One Tree Island Marina
Port of Olympia
East Bay Marina
Port of Olympia
East Bay Marina
Port of Olympia
29 January 1987 Provide public access., bank protection, and replacement of existing tide
grids; excavate 320 yd^ of bank material with upland disposal; place 190 yd
riprap and approximately 900 yd additional fill.
16 April 1982 Improve and expand moorage in commercial marina; 4,000 yd removed and
barged to East Bay fill site; 21,200 yd3 of dredged material deposited at
Dana Passage deep-water disposal site.
10 May 1983 Increase facility for commercial moorage; dredge approximately 6,000 ycr of
sand and gravel and dispose of on upland site; place approximately 150 yd
sand and gravel as fill.
7 January 1987 Provide additional boat moorage and adequate water depth; dredge approxi-
mately 33,700 ycr sand and^silt and dispose of at Steilacoom deep-water
disposal site; dredge 500 ycr contaminated material and dispose of at upland
site; two 4-ft sediment cores collected and analyzed; data analysis indicated
high concentrations of lead.
18 July 1986 Provide additional boat moorage; dredge 3,900 yd contaminated sediments;
excavate containment basin and dispose contaminated sedJments; cap contain-
ment basin with ^4 ft clean material; dredge 9,400 yd clean material and
dispose of at Steilacoom deep-water disposal site. Results of sediment
chemistry analyses are provided in Turpin and Associates (1985).
11 June 1981 Provide recreational boat moorage and launching facilities; permit expired
11 June 1985 and 70 percent of work was completed.
15 May 1981 Provide protection and adequate depth of water for boat movement within
marina, and to and from an existing navigation channel; fill to provide area
for cargo handling, parking, and marina support facilities; dredged
475,000 ydr organic silt and sand from moorage basin and place behind
retaining berm.
12 May 1987 Upgrade existing cargo area; dredge approximately 4,250 yd and dispose of on
upland site; place 8,000 tons riprap and 500 ycr backfill; upland disposal
site has not been identified yet, and work has not been completed (Malin
R., 25 November 1987, personal conrnunication).
U.S. ACOEC [No Date (a)]
U.S. ACOE [No Date (h)]
U.S. ACOE [No Date (b)]
U.S. ACOE [No Date (c)]
U.S. ACOE [No Date (d)]
U.S. ACOE [No Date (e)]
U.S. ACOE [No Date (k)]
U.S. ACOE [No Date (f)]
-------
TABLE C-1. (Continued)
Permittee3
Date
Permit Issued
Purpose
Reference
Tamoshan Homeowners
Association
Washington Department
of Fisheries
Washington Department
of Fisheries
15 June 1982
1 March 1982
3 June 1983
Erosion prevention; excavate and place 200 yd beach materials and 60 yd
coarse gravel adjacent to existing bulkhead (the gravel may not have been
deposited on the beach to protect surf smelt spawning areas).
Maintenance dredging in Capitol Lake; 1,500 ydr sediments deposited on
state-owned upland disposal site.
Erosion prevention in Deschutes River (immediately downstream of Capitol
Way).
U.S. ACOE [No Date (g)]
U.S. ACOE [No Date (i)]
U.S. ACOE [No Date (j)]
o
U.S. Army COE permit numbers are identified in the references. Permit number 071-OYB-2-006974 (Olvmpia Yacht Club) was not available for review.
1 U.S. Army COE, 27 October 1987, personal communication.
U.S. ACOE = U.S. Army Corps of Engineers.
-------
APPENDIX D
CONTAMINANT CONCENTRATIONS IN BUDD INLET SEDIMENTS
-------
TABLE D-1. CONTAMINANT CONCENTRATIONS IN BUDD INLET SEDIMENTS
Seq. Document Sample Sample
No. Number3 Number Date
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
39
40
41
42
43
44
45
46
47
48
49
50
51
52
53
54
55
56
57
58
59
60
61
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
1
1
1
1
1
1
2
2
2
2
2
2
3
3
3
3
3
3
3
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338035
338034
338034
338034
338034
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
4/23/86
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
Class
Number
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2.1
8
7
8
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2.1
8
7
8
1
1
1
1
Chemical Concentration
lead
copper
zinc
chromium
nickel
cadmium
lead
copper
zinc
chromium
nickel
cadmi urn
mercury
lead
copper
zinc
chromium
nickel
cadmium
acenaphthene
acenaphthylene
naphthalene
f luorene
anthracene
phenanthrene
f luoranthene
benzo(a)anthracene
chrysene
pyrene
benzof I uoranthenes
benzo(a)pyrene
dibenzo(a,h)anthracene
indeno(1,2,3-cd)pyrene
benzo(g,h, i )perylene
Total PAH
dibenzofuran
pentachlorophenol
2-methylnaphthalene
acenaphthene
acenaphthylene
naphthalene
f luorene
anthracene
phenanthrene
f luoranthene
benzo(a)anthracene
chrysene
pyrene
benzof I uoranthenes
benzo(a)pyrene
dibenzo(a,h)anthracene
indeno(1,2,3-cd)pyrene
benzo ( g , h , i ) pery I ene
Total PAH
dibenzofuran
pentachlorophenol
2-methylnaphthalene
acenaphthene
acenaphthylene
naphthalene
f luorene
9.2
0.0
29.3
3.7
2.7
0.0
33.4
106.0
116.9
55.6
41.7
5.6
0.2
6.5
47.0
112.0
43.1
25.0
0.0
100u
100u
100u
100u
100u
100u
220
100u
100u
660
100u
100u
100u
100u
100u
880
100u
100u
100u
20u
20u
94
20u
20u
120
330
20u
20u
630
330 j
20u
20u
20u
20u
1500
20u
20u
20u
2000
200u
170
730
D-1
-------
Seq. Document Sample Sannple
No. Number3 Nunber Date
62
63
64
65
66
67
68
69
70
71
72
73
74
75
76
77
78
79
80
81
82
83
84
85
86
87
88
89
90
91
92
93
94
95
96
97
98
99
100
101
102
103
104
105
106
107
108
109
110
111
112
113
114
115
116
117
118
119
120
121
122
123
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
338034
338034
338034
338034
338034
338034
338034
338034
338034
338034
338034
338034
338034
338034
338034
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
338036
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
79016
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
8/14/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
Class
Number
1
1
2
2
2
2
2
2
2
2
2
2.1
8
7
8
1
1
1
1
1
1
2
2
2
2
2
2
2
2
2
2.1
8
7
8
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
Chemical Concentration
anthracene
phenanthrene
f luoranthene
benzo(a)anthracene
chrysene
pyrene
benzof luoranthenes
benzo(a)pyrene
dibenzo(a,h)anthracene
indeno(1,2,3-cd)pyrene
benzo(g,h, i )perylene
Total PAH
dibenzofuran
pentach lorophenol
2-methylnaphthalene
acenaphthene
acenaphthylene
naphthalene
f luorene
anthracene
phenanthrene
f luoranthene
benzo(a)anthracene
chrysene
pyrene
benzof I uoranthenes
benzo(a)pyrene
dibenzo(a,h)anthracene
indeno(1,2,3-cd)pyrene
benzo(g,h, i )perylene
Total PAH
dibenzofuran
pentach lorophenol
2-methylnaphthalene
benzene
ethylbenzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof I uoranthenes
benzo(a)pyrene
indeno(1,2,3-cd)pyrene
benzo(g,h, i )perylene
phenol
2-methylphenol
4-methylphenol
2,4-dimethylphenol
pentach lorophenot
bis(2-ethylhexyl)phthalate
chlorobenzene
copper
1200
2000
6300
1600
2000
4200
1500
810
200u
200u
200u
23000
880
200u
200u
140
50u
39j
69
50u
630
1300
390 j
540 j
980
50u
50u
50u
50u
50u
4100
50u
50u
50u
9u
18
9u
9u
5800
790
330
14000
5300
5200
20000
2700
32000
20000
8000
8300
6600
100u
100J
100J
100u
100u
100u
100u
100u
760
9u
86.3
D-2
-------
Seq. Document Sample Sample Class
No. Number3 Number Date Number
124
125
126
127
128
129
130
131
132
133
134
135
136
137
138
139
140
141
142
143
144
145
146
147
148
149
150
151
152
153
154
155
156
157
158
159
160
161
162
163
164
165
166
167
168
169
170
171
172
173
174
175
176
177
178
179
180
181
182
183
184
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
79016
79016
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79017
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
79018
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
10
10
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
10
10
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
10
Chemical Concent rationb
chromium
arsenic
benzene
ethylbenzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof I uorant henes
benzo(a)pyrene
indenoC 1 ,2,3-cd)pyrene
benzo(g,h, i )perylene
pheno I
2-methylphenol
4-methylphenol
2,4-dimethylphenol
pentachlorophenol
bis(2-ethylhexyl)phthalate
chtorobenzene
copper
chromium
arsenic
benzene
ethylbenzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof 1 uo rant henes
benzo(a)pyrene
indeno(1,2,3-cd)pyrene
benzo(g,h, i )perylene
phenol
2-methylphenol
4-methylphenol
2,4-dimethylphenol
pentachlorophenol
bis(2-ethylhexyl )phthalate
chlorobenzene
copper
chromium
38.8
8
4j
510
48
400
210000
15000
400u
370000
130000
200000
800000
150000
530000
400000
95000
120000
73000
40000
400u
400u
400u
400u
400u
400u
400u
15000
8u
69.6
35
5.7
7u
7u
7u
7u
7200
640
400u
4800
1400
1300
2900
5700
42000
27000
7500
9700
6900
2700
400u
400u
400u
400u
400u
400u
400u
1100
7u
131.5
40.2
D-3
-------
Seq. Document Sample Sample Class
No. Number3 Number Date Number
185
186
187
188
189
190
191
192
193
194
195
196
197
198
199
200
201
202
203
204
205
206
207
208
209
210
211
212
213
214
215
216
217
218
219
220
221
222
223
224
225
226
227
228
229
230
231
232
233
234
235
236
237
238
239
240
241
242
243
244
245
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
79018
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79019
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
79020
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
10
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
10
10
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
10
10
Chemical Concentration
arsenic
benzene
ethylbenzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof luoranthenes
benzo(a)pyrene
indenod ,2,3-cd)pyrene
benzo(g,h,i )perylene
phenol
2-methylphenol
4-methylphenol
2,4-dimethylphenol
pentachlorophenol
bis(2-ethylhexyl)phthalate
chlorobenzene
copper
chromium
arsenic
benzene
ethylbenzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof I uoranthenes
benzo(a)pyrene
indeno(1,2,3-cd)pyrene
benzo(g,h, i )perylene
phenol
2-methylphenol
4-methylphenol
2,4-dimethylphenol
pentachlorophenol
bis(2-ethylhexyl)phthalate
chtorobenzene
copper
chromium
arsenic
10.7
5u
5u
5u
5u
3500
640
100j
1500
310
670
2000
650
3100
4300
670
740
880
360
100u
100u
100u
100u
120
100u
100u
100u
5u
37.4
20.5
11
5u
5u
5u
5u
9600
560
100j
620
250
300
1100
360
1300
1500
330
410
510
190
100u
100u
100u
100u
100u
100u
100u
120
5u
32
20.2
5.5
D-4
-------
Seq. Document Sample Sanple Class
No. Number3 Number Date Number
246
247
248
249
250
251
252
253
254
255
256
257
258
259
260
261
262
263
264
265
266
267
268
269
270
271
272
273
274
275
276
277
278
279
280
281
282
283
284
285
286
287
288
289
290
291
292
293
294
295
296
297
298
299
300
301
302
303
304
305
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79021
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
79022
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
10
10
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
10
10
Chemical Concentration
benzene
ethyl benzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof I uoranthenes
benzo(a)pyrene
indenod ,2,3-cd)pyrene
benzo(g,h,i)perylene
phenol
2-methylphenol
4-methylphenol
2, 4 -dimethyl phenol
pentachlorophenol
bis(2-ethylhexyl)phthalate
chlorobenzene
copper
chromium
arsenic
benzene
ethylbenzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof luoranthenes
benzo(a)pyrene
indenod, 2, 3-cd)pyrene
benzo(g,h,i)perylene
phenol
2-methylphenol
4-methylphenol
2,4-dimethylphenol
pentachlorophenol
bis(2-ethylhexyl)phthalate
chlorobenzene
copper
chromium
arsenic
7u
7u
7u
7u
2400
200u
200u
660
220
200u
1300
820
7300
450
3500
1900
1600
750
200u
200u
200u
200u
200u
200u
200u
640
7u
62.6
35.2
7.6
5u
5u
5u
5u
530
100J
100J
190
78j
82 j
400
300
4900
3800
1300
1800
1600
680
100u
100u
100u
100u
100u
100u
100u
420
5u
71.5
35.2
7.3
D-5
-------
Seq. Document Sample Sample
No. Number3 Number Date
306
307
308
309
310
311
312
313
314
315
316
317
318
319
320
321
322
323
324
325
326
327
328
329
330
331
332
333
334
335
336
337
338
339
340
341
342
343
344
345
346
347
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
3
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79023
79017
79017
79017
79017
79019
79019
79019
79019
79020
79020
79020
79020
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
2/13/85
Class
Number
99
9
99
9
1
8
1
1
8
1
1
1
2
2
2
2
2
2
2
2
7
7
7
7
7
5
99
10
10
10
8
8
8
8
8
8
8
8
8
8
8
8
Chemical Concentration
benzene
ethyl benzene
toluene
total xylenes
naphthalene
2-methylnaphthalene
acenaphthylene
acenaphthene
dibenzofuran
f luorene
phenanthrene
anthracene
f luoranthene
pyrene
benzo(a)anthracene
chrysene
benzof I uoranthenes
benzo(a)pyrene
indeno(1,2,3-cd)pyrene
benzo(g,h,i )perylene
phenol
2-methylphenol
4-methylphenol
2,4-ditnethylphenol
pentachlorophenol
bis(2-ethylhexyl)phthalate
chlorobenzene
copper
chromium
arsenic
1-methylnaphthalene
2-methylnaphthalene
dibenzothiophene
biphenyl
1-methylnaphthalene
2-methylnaphthalene
d i benzoth i ophene
biphenyl
1-methylnaphthalene
2-methylnaphthalene
dibenzothiophene
biphenyl
5u
54
5u
5u
100u
100u
100u
100u
100u
100u
100u
100u
220
660
lOOu
100u
100u
100u
100u
100u
lOOu
100u
100u
100u
100u
1600
10
56.6
20.6
9
780000
270000
2800
540
2100
910
Reference: 1. Alan, R. (24 September 1987, personal communication).
2. Norton, D. (5 February 1986, personal communication).
3. Johnson, A. (22 July 1985, personal communication).
' Expressed in mg/kg dry wt for trace metals and ug/kg dry wt for organic substances.
D-6
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APPENDIX E
BUDD INLET BIBLIOGRAPHY
-------
BUDD INLET BIBLIOGRAPHY
Advanced Engineering. 6 June 1986. Personal Communication (information to
Dunlap Towing Company, Olympia, WA; chip storage pile dust analysis,
Appendix 1-2 through 1-7 to Olympia Staff/Committee Report for Olympia
Planning Department file number SH-OLY-3-85). Advanced Engineering,
Olympia, WA.
Alan, R. 24 September 1987a. Personal Communication (information to Ms.
Karen L. Keeley; Budd Inlet sample survey, Department of Public Works, City
of Olympia). LOTT Sewage Treatment Facility, Olympia, WA. 12 pp.
Alan, R. 24 September 1987b. Personal Communication (information to Ms.
Karen L. Keeley; draft 1988 monitoring program of the LOTT facility,
Olympia, WA). LOTT Sewage Treatment Facility, Olympia, WA. 2 pp.
Alan, R. 19 January 1988. Personal Communication (phone by Ms. Karen L.
Keeley; information on LOTT's outfalls). LOTT Sewage Treatment Facility,
Olympia, WA.
Alan, R. 9 February 1988. Personal Communication (phone by Ms. Betsy Day;
information on effluent bioassays conducted by LOTT). LOTT Sewage Treatment
Facility, Olympia, WA.
Alan, R. 14 March 1988. Personal Communication (phone by Ms. Karen L.
Keeley; information on historical landfill located near LOTT facility).
LOTT Sewage Treatment Facility, Olympia, WA.
Alan, R. 25 March 1988. Personal Communication (phone by Ms. Karen L.
Keeley). LOTT sewage treatment facility, Olympia, WA.
Anderson, D. 22 December 1986. Personal Communication (letter to Mr.
Dennis 0. Cole, Industrial Petroleum Distributors, Inc., Tacoma, WA; Olympia
facility, contaminated soils, Ecology Order No. DE 86-S133). Washington
Department of Ecology, Olympia, WA. 2 pp.
Anderson, D. 29 October 1987. Personal Communication (phone by Ms. Karen
L. Keeley; Budd Inlet). Washington Department of Ecology, Olympia, WA.
1 pp.
Anderson, D. 6 April 1988. Personal Communication (phone by Ms. Karen L.
Keeley). Washington Department of Ecology, Olympia, WA.
Applied Geotechnology. 1986a. Volume I. Remedial investigation, Cascade
Pole Company, Olympia, Washington. AGI Job No. 14,825.104. Prepared for
McFarland Cascade, Cascade Pole Company, Olympia, WA. Applied Geotechnology,
Inc., Bellevue, WA. 103 pp.
E-l
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Applied Geotechnology. 1986b. Volume II. Remedial investigation-
appendices, Cascade Pole Company, Olympia, Washington. AGI Job No.
14,825.104. Prepared for McFarland Cascade, Cascade Pole Company, Olympia,
WA. Applied Geotechnology, Inc., Bellevue, WA.
Applied Geotechnology. 1987. Intertidal sediment study: polycyclic
aromatic hydrocarbons and phenols, Cascade Pole Company, Olympia, Washington.
AGI Project No. 14,825.107. Prepared for Cascade Pole Company, Olympia,
WA. Applied Geotechnology, Inc., Bellevue, WA.
Arden, H. 26 January 1988. Personal Communication (phone by Ms. Karen L.
Keeley). U.S. Army Corps of Engineers, Seattle, WA.
Arden, H. 10 February 1988. Personal Communication (phone by Ms. Betsy
Day; information concerning sediment resuspension by the East Bay Marina
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Arden, H. 11 February 1988. Personal Communication (phone by Ms. Betsy
Day; criteria for operation of East Bay Marina aeration system). U.S. Army
Corps of Engineers, Seattle, WA.
Armstrong, J. 17 November 1987. Personal Communication (information to Ms.
Karen L. Keeley; microbiological sample results for fecal coliforms/100 gm
shellfish tissue, 30 June 1987, Washington Department of Social and Health
Services and U.S. Environmental Protection Agency study). U.S. Environmental
Protection Agency Region X, Seattle, WA. 3 pp.
Arvid Grant and Associates. 1973. Water pollution control and abatement
plan for Deschutes River basin. State of Washington Water Resources
Inventory Area No. 13 in Thurston and Lewis Counties. Prepared for Thurston
Regional Planning Council, Olympia, WA. Arvid Grant and Associates, Inc.,
Olympia, WA. 117 pp. + 15 figures and appendix.
Babcock, S. 6 October 1987. Personal Communication (phone by Ms. Karen L.
Keeley). U.S. Army Corps of Engineers, Engineering Division, Seattle, WA.
Barghausen Consulting Engineers. 7 August 1986. Personal Communication
(letter to Mr. Gary Kato, Thurston County Health Department, Environmental
Health Division, Olympia, WA; disposal of solid waste material/proposed ARCO
FAC #5301, State Street and East Bay, Olympia, WA). Barghausen Consulting
Engineers, Inc., Kent, WA. 6 pp.
Bauchman, J.W. 1974. Saving a beautiful lake: an overview of the economic
and recreational benefits of reclamation and proposed recreational profiles
for the future of Capitol Lake and the visual basin. Olympia, WA. 35 pp.
Bernhardt, J. 13 August 1981. Personal Communication (memorandum to Mr.
Jim Krull, Washington Department of Ecology; Budd Inlet fish kill).
Washington Department of Ecology, Olympia, WA. 19 pp.
Bernhardt, J., and B. Yake. 22 June 1983. Personal Communication (memo-
randum to Mr. Frank Monahan, Washington Department of Ecology; LOTT Phase II
E-2
-------
receiving water considerations).
WA. 15 pp.
Washington Department of Ecology, Olympia,
Black & Veatch. 1987. Cascade Pole Company feasibility study work plan.
Prepared for Washington Department of Ecology, Olympia, WA. Black & Veatch,
Olympia, WA, and Tetra Tech, Inc., Bellevue, WA. 49 pp.
Bradley, D. 12 January
Richard Pierce, Thurston
Division, Olympia, WA).
33 pp.
1987a. Personal Communication (letter to Mr.
County Health Department, Environmental Health
Washington Department of Ecology, Olympia, WA.
Bradley, D. 12 January 19875. Personal Communication (memorandum to
McFarland Cascade file; potential health risks associated with consumption
of shellfish from Budd Inlet). Washington Department of Ecology, Olympia,
WA. 3 pp.
Bradley, D. 30 March 1988. Personal Communication (phone by Mr. J.
Portele). Washington Department of Ecology, Olympia, WA.
Calambokidis, J., J. Peard, G.H. Steiger, and J.C. Cubbage. 1984. Chemical
contaminants in marine mammals from Washington State. NOAA Technical
Memorandum NOS QMS 6. National Oceanic and Atmospheric Administration,
National Ocean Service, Rockville, MD. 167 pp. including appendices.
Calambokidis, J., S.H. Speich, J.
Fry, and L.J. Lowenstine. 1985.
marine birds: population health
Technical Memorandum NOS DMA 18.
stration, National Ocean Service,
dices.
Peard, G.H. Steiger, J.C. Cubbage, D.M.
Biology of Puget Sound marine mammals and
and evidence of pollution effects. NOAA
National Oceanic and Atmospheric Admini-
Rockville, MD. 159 pp. including appen-
Capitol Lake Restoration Committee. 1987. Capitol
Capitol Lake Restoration Committee, Olympia, WA. 57 pp.
Lake action plan.
+ appendices.
CH2M Hill. 1978. Water quality in Capitol Lake, Olympia, Washington.
Prepared for Washington Department of Ecology and Washington Department of
General Administration. CH2M Hill, Bellevue, WA. 79 pp. + appendices.
CH2M. 1972. Thurston County: a comprehensive water and sewerage plan.
Volume III sewerage plan. CH2M, Bellevue, WA. 57 pp. + appendices.
Clark, D. 21 November 1985. Personal Communication (memorandum to Mr.
Darrel Anderson, Washington Department of Ecology, Southwest Regional
Office; Beverly Beach wastewater treatment plant limited Class II inspection,
June 17-18, 1985). Washington Department of Ecology, Olympia, WA. 12 pp.
Clark, D. 27 January 1986. Personal Communication (memorandum to Mr.
Darrel Anderson, Washington Department of Ecology, Southwest Regional
Office; Tamoshan wastewater treatment plant limited Class II inspection,
June 17-18, 1985). Washington Department of Ecology, Olympia, WA. 13 pp.
E-3
-------
Clark, D. 25 March 1986. Personal Communication (memorandum to Mr. Darrel
Anderson, Washington Department of Ecology, Southwest Regional Office;
Seashore Villa wastewater treatment plant limited Class II inspection, July
1-2, 1985). Washington Department of Ecology, Olympia, WA. 11 pp.
Cloud, G. 30 October 1987. Personal Communication (phone by Ms. Karen L.
Keeley; Budd Inlet Industrial Petroleum Distributors, Inc., waste oil
spill). Washington Department of Ecology, Olympia, WA. 1 pp.
Colby, J. 28 March 1988. Personal Communication (phone by Ms. Karen L.
Keeley). LOTT Sewage Treatment Facility, Olympia, WA.
Collias, E., et al. 1962. Physical and chemical data for southern Puget
Sound, August 1957-October 1958. University of Washington, Department of
Oceanography Technical Report No. 67.
Cox, J.M., C.C. Ebbesmeyer, C.A. Coomes, L.R. Hinchey, J.M. Helseth, G.A.
Cannon, and C.A. Barnes. 1981. Index to observations of currents in Puget
Sound, Washington, from 1908-1980. NOAA Technical Memorandum OMPA-5.
National Oceanic and Atmospheric Administration, Office of Marine Pollution
Assessment, Boulder, CO. 51 pp. including appendices.
Cunningham, J. 21 September 1987. Personal Communication (phone by Ms.
Karen L. Keeley). City of Olympia Engineering Department, Olympia, WA.
Dames & Moore. 1973. Report of soils investigation, proposed East Bay
development program, Port of Olympia, Olympia, Washington. Prepared for
Port of Olympia, Olympia, WA. Dames & Moore, Seattle, WA. 18 pp. + plates
and appendices.
Dames & Moore. 1974. Report of bottom sediment sampling and analyses,
proposed East Bay dredging and landfill, Olympia, Washington. Prepared for
Port of Olympia, Olympia, WA. Dames & Moore, Seattle, WA. 11 pp. + tables.
Department of Social and Health Services. 1987. Chemicals and bacterio-
logical organisms in non-commercial shellfish. Draft Report. DSHS,
Olympia, WA.
Determan, T. 19 February 1981. Personal Communication (memorandum to Mr.
John Bernhardt, Washington Department of Ecology; effects of Tamoshan STP
outfall on water quality at Silver Spit, Budd Inlet). Washington Department
of Ecology, Olympia, WA. 10 pp.
Determan, T. 5 March 1981. Personal Communication (memorandum to Mr. John
Bernhardt, Washington Department of Ecology; effects of Tamoshan STP outfall
on water quality at Silver Spit, Budd Inlet). Washington Department of
Ecology, Olympia, WA. 8 pp.
Devitt, R.C. 2 June 1983. Personal Communication (memorandum to Mr. Ron
Robinson, Mr. Mike Pierce, and Mr. Gene Asselstine, Washington Department of
E-4
-------
Ecology; Olympia STP, Budd Inlet dye survey and
Washington Department of Ecology, Southwest Regional
17 pp.
aerial photographs).
Office, Olympia, WA.
Dexter, R.N., D.E. Anderson, E.A. Quinlan, L.S. Goldstein, R.M. Strickland,
S.P. Pavlou, J.R. Clayton, Jr., R.M. Kocan, and M. Landolt. 1981. A
summary of knowledge of Puget Sound related to chemical contaminants. NOAA
Technical Memorandum OMPA-13. National Oceanic and Atmospheric Admini-
stration, Office of Marine Pollution Assessment, Boulder, CO. 435 pp.
Dexter, R.N., L.S. Goldstein, P.M. Chapman, and E.A. Quinlan. 1985.
Temporal trends in selected environmental parameters monitored in Puget
Sound. NOAA Technical Memorandum NOS OMA 19. National Oceanic and Atoms-
pheric Administration, National Ocean Service, Rockville, MD. 166 pp.
Duxbury, A.C., M.A. Freibertshauser, and E.P. Richey. 1972. Budd Inlet
circulation and flushing study. Appendix A. Submitted to Arvid Grant and
Associates, Inc., Olympia, WA. 12 pp.
Earth Consultants. 1985. Supplemental soil hydrocarbon content evaluation,
proposed Arco station, East Bay Drive and State Avenue, Olympia, WA.
Prepared for Barghausen Consulting Engineers, Inc., Kent, WA. Earth
Consultants, Inc., Bellevue, WA. 11 pp. + tables.
Earth Consultants. 7 August 1986. Personal Communication (letter to Mr. Al
Kendall, Barghausen Consulting Engineers, Kent, WA; supplemental chemical
analysis of soils, proposed Arco station, East Bay Drive and State Avenue,
Olympia, WA). Earth Consultants, Inc., Bellevue, WA. 2 pp.
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Karen L. Keeley; Port of Olympia properties). Port of Olympia, WA.
Egge, E. 25 January 1987. Personal Communication (information to Ms. Karen
L. Keeley; Port of Olympia East Bay Marina dissolved oxygen monitoring
data). Port of Olympia, Olympia, WA.
Egge, E. 1 February 1988. Personal Communication (phone by Ms. Betsy Day;
information on operation of East Bay Marina aeration system). Port of
Olympia, WA.
Entrance Engineers. 1983. Capitol Lake restoration analysis. Prepared for
Washington Department of General Administration. Entrance Engineers,
Bellevue, WA. 128 pp. + appendices.
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Cascade Pole Company site, Olympia, Washington. Document No. P-E464-200.
E-5
-------
Prepared for Cascade Pole Company, Olympia, WA. ERT, Concord, MA. 68 pp.
+ appendices.
ERT. 30 April 1987. Personal Communication (letter to Mr. David A. Bradley,
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Evans-Hamilton and D.R. Systems. 1987. Puget Sound environmental atlas.
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polychlorinated biphenyls in the benthic community. The Evergreen State
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Faigenblum, J. 17 November 1987. Personal Communication (phone by Ms.
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Fall 1987). Washington Department of Social and Health Services, Shellfish
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GeoEngineers. 1987. Dredge spoil evaluation, Berth 3 reconstruction,
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E-6
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Helmlinger, J. 23 March 1988. Personal Communication (phone by Ms. Karen
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Karen L. Keeley; Capitol Lake siphon system and water quality monitoring).
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quality measurements in Budd Inlet, July 2, 1981). Washington Department of
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Johnson, A. 22 July 1985. Personal Communication (memorandum to Mr. Tom
Eaton, Washington Department of Ecology; receiving environment survey in
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of Ecology, Olympia, WA. 7 pp.
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Bernhardt, Washington Department of Ecology; sulfide concentrations in
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Ecology, Olympia, WA. 10 pp.
JRB Associates. 1984. Water quality dependent water uses in Puget Sound.
Final Report. Prepared for U.S. Environmental Protection Agency, Washington
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(memorandum to Mr. Tom Eaton, Washington Department of Ecology; effects of
three small sewage treatment plants on Budd Inlet receiving waters).
Washington Department of Ecology, Olympia, WA. 22 pp.
Kessler, F. 18 December 1987. Personal Communication (letter to Ms. Karen
L. Keeley; LOTT wastewater treatment plant receiving water sampling program
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figures.
Kittle, L. 29 January 1988. Personal Communication (phone by Ms. Karen L.
Keeley). Washington Department of Ecology, Olympia, WA.
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Washington Department of Ecology, Olympia, WA. 23 pp.
E-7
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Konasewich, D.E., P.M. Chapman, E. Gerencher, G. Vigers, and N. Treloar.
1982. Effects, pathways, processes, and transformation of Puget Sound
contaminants of concern. NOAA Technical Memorandum OMPA-20. National
Oceanic and Atmospheric Administration, Office of Marine Pollution Assess-
ment, Boulder, CO. 357 pp.
Kramer, Chin & Mayo. 1973. An engineering study of the Percival Creek
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Inc., Seattle, WA. 46 pp. + appendices.
Kramer, Chin & Mayo. 1975. Receiving-water quality objectives. Prepared
for Lacey, Olympia, Tumwater, and Thurston County (LOTT) Complex Facility
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Inc., Seattle, WA. 28 pp. including appendix.
Kruger, D.M. 1979. Effects of point-source discharges and other inputs on
water quality in Budd Inlet, Washington. DOE 79-11. Washington Department
of Ecology, Olympia, WA. 40 pp. + appendices.
Lilja, J. 25 March 1988. Personal Communication (phone by Ms. Betsy Day).
Washington Department of Social and Health Services, Olympia, WA.
Mai in, D. 18 November 1987. Personal Communication (information to Ms.
Karen L. Keeley; Port of Olympia ownerships in Budd Inlet). Port of Olympia,
Olympia, WA. 1 pp.
Mai in, D. 25 November 1987. Personal Communication (phone by Ms. Karen L.
Keeley; information on dredging permit 071-OYB-2-010937). Port of Olympia,
Olympia, WA.
Malins, D.C., B.B. McCain, D.W. Brown, A.K. Sparks, and H.O. Hodgins. 1980.
Chemical contaminants and biological abnormalities in central and southern
Puget Sound. NOAA Technical Memorandum OMPA-2. National Oceanic and
Atmospheric Administration, Office of Marine Pollution Assessment, Boulder,
CO. 295 pp. including appendices.
Malins, D.C., B.B. McCain, D.W. Brown, A.K. Sparks, H.O. Hodgins, and S.-
L. Chan. 1982. Chemical contaminants and abnormalities in fish and invert-
ebrates from Puget Sound. NOAA Technical Memorandum OMPA-19. National
Oceanic and Atmospheric Administration, Office of Marine Pollution Assess-
ment, Boulder, CO. 168 pp. including appendix.
McCallum, M. 1985. Recreational and subsistence catch and consumption of
seafood from three urban industrial bays of Puget Sound: Port Gardner,
Elliot Bay and Sinclair Inlet. Washington State Department of Social and
Health Services, Division of Health, Epidemiology Section, Olympia, WA.
59 pp. including appendices.
McCarthy, B. 15 January 1988. Personal Communication (phone by Ms. Lynne
M. Kilpatrick-Howard). City of Olympia, Public Works Department, Olympia,
WA.
E-8
-------
McNicholas, R. 1984. Stream corridor management plan for the Deschutes
River, Washington. Project No. 82-145A. Prepared for Washington State
Department of General Administration, Olympia, WA. Thurston County Con-
servation District, Olympia, WA. 65 pp,
,.j...r.-, WA. Thurston
including appendices.
Mih, W.C. 1976. Supplemental flow and sediment
hydraulic model. Prepared for Washington State
Administration, Olympia, WA. Washington State University, College
Engineering, Albrook Hydraulics Laboratory, Pullman, WA. 11 pp.
tests of Capitol Lake
Department of General
of
Moore, A. 13 April 1982. Personal Communication (memorandum to Ms.
Thomas, Washington Department of Ecology; outfall sampling to Capitol
during March 1982 drawdown). Washington Department of Ecology, Olympia
6 pp.
Joan
Lake
WA.
Moore, D. 17 November 1987. Personal Communication
Keeley; City of Olympia combined sewer overflow
Olympia, Engineering Department, Olympia, WA.
Moore, D. 9 December 1987. Personal Communication
Keeley; City of Olympia combined sewer overflow.
Olympia, Engineering Department, Olympia, WA.
(phone by Ms. Karen L.
locations). City of
(letter to Ms.
locations).
Karen L.
City of
Moore, D. 29 March 1988. Personal Communication (phone by Ms. Karen L.
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