EPA 910-9-76-029
1976
REGION X
1200 SIXTH AVENUE
SEATTLE, WASHINGTON 98101
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EPA-910/9-76-029
September 1976
CHEMICAL AND BIOLOGICAL SURVEY
OF LIBERTY BAY, WASHINGTON
by
Joseph M. Cummins
Ralph R. Bauer
Robert H. Rieck
William B. Schmidt
John R. Yearsley
U.S. ENVIRONMENTAL PROTECTION AGENCY
REGION X
SURVEILLANCE AND ANALYSIS DIVISION
SEATTLE, WASHINGTON 98101
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DISCLAIMER
This report has been reviewed by Region X, U.S. Environmental
Protection Agency, and approved for publication. Mention of trade
names or commercial products does not constitute endorsement or
recommendation for use.
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TABLE OF CONTENTS
INTRODUCTION
Page
1
Purpose
. . . . . I
2
SUMMARY
3
Findings and Conclusions
Recommendations . . . .
0 3
. . . • • • . . 6
DESCRIPTION OF STUDY AREA
Location and General Use . .
Hydrography and Circulation .
Sediments
Fisheries Resources .
Water Characteristics
Temperature
Salinity
Nutrients . . . .
Dissolved Oxygen
Point Source Discharges
METHODS . . . .
8
21
Field Activities
Sampling..
Water
Sediment
Fish
Shellfish . . . .
Hydrographic Measurements
Laboratory Activities
Chemical
Biological . . . . . .
Oyster Embryo Bioassay
Sample Preparation
Water .
Sediment
STP Effluent
21
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I I I I I S I I S I I
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Nonpoint Source Discharges and Other Activities
Oyster Spawning and Sample Inoculation
Termination . . . . . . • . • . •
Larval Enumeration • •
Bioassay Evaluation
Plankton Identification and Enumeration .
Compliance Monitoring Inspection • . • . . . • . •
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TABLE OP CONTENTS (Continued)
Page
RESULTSANDDISCUSSION.................... 30
Chemical and Physical Characteristics
Water
General Conditions
Metal Concentrations . .
Sediments
Metal Concentrations
Surface Sediments
Sediment Cores
Organochiorine Compounds in Surface
Sulf ides in Surface Sediments
Shellfish
Metal Concentrations
Interspecific Differences
Distribution . . . .
Comparative Data
Organochiorine Concentrations
Fish Muscle Tissue . . . .
Metal Concentrations
Biological Characterization . . . .
Phytoplankton Production
Oyster Embryo Response . . . .
Water
Survival.........
Development . .
Sediment
Sewage Treatment Plant Effluents
Biological Significance of Various Chemical
and Biological Factors
Mercury..
OtherMetals
Sewage Treatment Plant Effluents
Phytoplankton, Bacteria, and Fungi
REFERENCES . . . . . . . . . .
APPENDIX A — Washington State Water Quality Standards
APPENDIX B — Point Source Loadings to Liberty Bay
• • 30
30
30
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37
38
38
57
Sediments . . 61
63
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63
. 63
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• . • 67
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. 85
85
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. 87
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91
91
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99
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106
108
109
• • • . • 113
• . . . • 117
• . . . . 123
. . . . . 129
132
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LIST OF FIGURES
Fig re Page
1 Location of Liberty Bay and survey reference 9
stat ions
2 Port Orchard oceanographic system 10
3 Currents within the Liberty Bay system during 12
maximum ebb and flood tides
A Surface sediment characteristics within the 13
Liberty Bay system
5 Location of waste treatment facilities and major 18
discharge points within the Liberty Bay system
6 Location of sampling stations 22
7 Antimony concentrations in Liberty Bay surface 41
sediments (ug/g dry weight)
8 Arsenic concentrations in Liberty Bay surface 42
sediments (ug/g dry weight)
9 Cadmium concentrations in Liberty Bay surface 44
sediments (ugfg dry weight)
10 Chromium concentrations in Liberty Bay surface 46
sediments (ug/g dry weight)
II Copper concentrations in Liberty Bay surface 47
sediments (ug/g dry weight)
12 Iron concentrations in Liberty Bay surface 49
sediments (mg/g dry weight)
13 Lead concentrations in Liberty Bay surface 50
sediments (ug/g dry weight)
14 Manganese concentrations in Liberty Bay surface 52
sediments (ug/g dry weight)
15 Mercury concentrations In Liberty Bay surface 53
sediments (ug/g dry weight)
16 Nickel concentrations in Liberty Bay surface 56
sediments (ug/g dry weight)
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LIST OF FIGURES (Continued)
Figure Page
17 Zinc concentrations in Liberty Bay surface 58
sediments (ug/g dry weight)
18 Total sulfide concentrations in Liberty Bay 64
surface sediments (ug/g dry weight)
19 Antimony concentrations in several species of 68
Liberty Bay shellfish (ug/g wet weight)
20 Arsenic concentrations in several species of 69
Liberty Bay shellfish (ug/g wet weight)
21 Cadmium concentrations in several species of 70
Liberty Bay shellfish (ug/g wet weight)
22 Chromium concentrations in several species of 71
Liberty Bay shellfish (ug/g wet weight)
23 Copper concentrations in several species of 72
Liberty Bay shellfish (ug/g wet weight)
24 Lead concentrations in several species of 73
Liberty Bay shellfish (ug/g wet weight)
25 Mercury concentrations in several species of 74
Liberty Bay shellfish (ug/g wet weight)
26 Nickel concentrations in several species of 75
Liberty Bay shellfish (ug/g wet weight)
27 Selenium concentrations in several species of 76
Liberty Bay shellfish (ug/g wet weight)
28 Zinc concentrations in several species of 77
Liberty Bay shellfish (ug/g wet weight)
29 Relative per cent survival of Pacific oyster 94
embryos in Liberty Bay waters collected during
low tide
30 Relative per cent survival of Pacific oyster 96
embryos in Liberty Bay waters collected during
high tide
31 Per cent abnormal development of Pacific oyster 98
embryos in Liberty Bay waters collected during
low tide
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LIST OF FIGURES (Continued)
Figure Page
32 Per cent abnormal development of Pacific oyster 100
embryos in Liberty Bay waters collected during
high tide
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LIST OF TABLES
Table Page
1 Analytical methods followed during survey of 26
Liberty Bay
2 General physical and chemical properties of 31
Liberty Bay, Clam Bay, and Hood Canal waters
3 Concentrations of metals in surface sediments 39
from Liberty Bay, Clam Bay, and Hood Canal
4 Concentrations of metals in sediment cores 59
collected from Liberty Bay
5 Concentrations of several organochlorine compounds 62
in Liberty Bay and Clam Bay surface sediments
6 Concentrations of metals in shellfish collected 65
from Liberty Bay, Clam Bay, and Hood Canal
7 Concentrations of metals in Japanese littleneck 79
clams, Venerupis japonica , from Liberty Bay,
Hood Canal, and other west coast locations
8 Concentrations of metals in native littleneck 80
clams, Venerupis staminea , from Liberty Bay,
Clam Bay, and other west coast locations
9 Concentrations of metals in butter clams, 81
Saxidomus giganteus , from Liberty Bay and
other west coast locations
10 Concentrations of metals in Pacific oysters, 82
Crassostrea gigas , from Liberty Bay and other
west coast locations
11 Concentrations of polychlorinated biphenyls in 84
shellfish collected from Liberty Bay
12 Concentrations of metals in the muscle tissue 86
of bottom fishes collected from Liberty Bay,
Clam Bay, and Hood Canal
13 Pacific oyster embryo survival (48—hour) in 92
Liberty Bay, Clam Bay, and Hood Canal waters
14 Pacific oyster embryo development (48—hour) in 93
Liberty Bay, Clam Bay, and Hood Canal waters
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LIST OF TABLES (Continued)
Table Page
15 Pacific oyster embryo responses as related to 97
total organic carbon levels in Liberty Bay waters
16 Pacific oyster embryo responses (48—hour) to 102
seawater suspensions of Liberty Bay surface
sediments
17 Pacific oyster embryo responses (48—hour) asso— 104
dated with actual concentrations of metals,
total sulfides, and total volatile solids
contributed by 10 g/l (wet weight) sediment
treatments
18 Pacific oyster embryo responses (48—hour) to 105
treated effluents from three sewage treatment
plants discharging into Liberty Bay or nearby
waters
19 Estimated number of acute toxic units discharged 107
daily to the Liberty Bay system by local sewage
treatment plants
20 Estimated total metal concentrations in Liberty 110
Bay seawater resulting from bypassing plating
wastes at the Navy Torpedo Station, Keyport,
Washington
21 Estimated safe concentrations of various metals 114
to oyster embryos of the genus Crassostrea
22 Estimated minimum dilution of sewage treatment 115
plant effluents 1000 meters from their source
under different tidal speeds and diffusion rates
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ACKNOWLEDGEMENTS
This survey represented the combined efforts of a number of EPA
personnel as well as the assistance of private citizens and representa-
tives of municipal, State, and other Federal agencies.
Primary responsibility for the collection and analysis of samples
was shared by the Surveillance Branch and Laboratory Branch of the
Surveillance and Analysis Division, EPA—Region X. Illustrations
appearing in the report were prepared by the Graphics Unit of the
EPA—Region X, Support Services Branch.
The authors thank Drs. Richard Steele and Jan Prager of EPA’s
Narragansett Environmental Research Laboratory, Narragansett, Rhode
Island, for Identifying and photographing the major phytoplankton and
protozoan organisms present in Liberty Bay during and following the
survey. Also appreciated was the taxonomic help offered by Bob Matsuda
and Bob Brenner of METRO, Seattle, Washington. The Washington State
Department of Social and Health Services, the U.S. Food and Drug Admin-
istration, and the National Marine Fisheries Service kindly provided
comparative data on metals levels in shellfish from Liberty Bay. The
background information provided by personnel of the City of Poulsbo,
the College of Fisheries — University of Washington, Roats Engineering,
Sea Farms, Inc., the U.S. Navy, the Washington State Department of
Ecology, and the Washington State Department of Fisheries is also grate-
fully acknowledged.
Special thanks go to the Coast Oyster Company and to the many
private property owners who granted us permission to collect shellfish
samples from their beaches.
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INTRODUCT ION
An intensive chemical and biological survey of Liberty Bay,
Washington was launched by EPA, Region X in September, 1975 fol-
lowing reports of heavy metal contamination of the Bay’s surface
waters.
Concentrations of total mercury ranging from <1 ugh to as
high as 110 ugh were reportedly measured in Liberty Bay seawater
by a commercial testing laboratory in conjunction with a privately
financed water quality investigation. The investigation was initi-
ated by Sea Farms, Inc., an oyster hatchery located in Poulsbo,
Washington. The hatchery’s interest in the chemistry of Liberty
Bay seawater stemmed from its basic need for water of high quality
coupled with its desire to identify the cause of mortalities of
Pacific oyster embryos and larvae experienced at various times
since it began using Liberty Bay water in July, 1973.
During the period Sea Farms was plagued most heavily with larval
mortalities (October 1974 — August 1975) it began to suspect and
investigate several activities associated with the Bay as being
possible sources of the problem. These activities included the
hatchery operation itself, as well as the discharge of wastes from
the Poulsbo sewage treatment plant, the dredging of the Poulsbo
marina in the spring of 1975, and the discharge of metal—laden wastes
from the Navy’s Keyport Torpedo Station. After reporting the results
of the investigation, Sea Farms closed the hatchery in August, 1975,
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believing that mercury and possibly other metal contaminants were
responsible for the recurrent mortalities of the young oysters.
Purpose
The EPA survey was initiated to quickly obtain information on
the levels of heavy metals and other possible toxicants in seawater,
wastes, sediments, fish, and shellfish from selected sites in Liberty
Bay and other Puget Sound waters. The investigation was also designed
to provide toxicological data on the acute effects of these waters
and sediments on the development and survival of embryos of the
Pacific oyster, Crassostrea gigas . This descriptive information
was needed to achieve the following objectives:
1. Determine if Liberty Bay was seriously contaminated with mercury
or other metals as reported,
2. Identify and locate possible sources of such toxicants, thus pro-
viding evidence supporting required pollution control or enforce-
ment actions,
3. Provide public health officials with information on which to base
decisions concerning the harvesting and consumption of fish and
shellfish from the Liberty Bay area, and
4. Elucidate the role of Liberty Bay water quality in the reported
mortalities of Pacific oyster embryos and larvae.
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SUMMARY
(Findings and Conclusions)
1. A history of continuous or intermittent mercury contamina-
tion in Liberty Bay of the magnitude reported by Sea Farms, Inc.,
would undoubtedly have had an adverse effect on oyster embryos and
larvae in addition to seriously contaminating a variety of marine
organisms of ecologic and economic value. However, no major sources
of mercury or serious mercury contamination were found during the
survey. Total mercury concentrations in Liberty Bay seawater were
similar to those measured in east—central Hood Canal — an area con-
sidered to be relatively free of industrial pollutants. The concen-
trations of mercury measured in marine organisms from the Bay also
suggested that serious mercury contamination was not a persistent
problem. Mercury levels in edible tissues of fish and shellfish
collected from Liberty Bay were below the proposed FDA Action Level
of 0.5 ug/g (wet weight) for mercury in seafoods.
2. Elevated concentrations of mercury and several other metals
were measured, however, in sediments from several Liberty Bay sites.
This apparent contamination was believed to reflect inputs of metallic
wastes to the Liberty Bay system resulting from inadequate industrial
and domestic waste treatment.
3. The Navy Torpedo Station was found in violation of its
National Pollution Discharge Elimination System (NPDES) permit. Sea
Farms, Inc. and the City of Poulsbo’s sewage treatment plant were
found In violation of the Federal Water Pollution Control Act (P.L.
92—500) for discharging wastewater to Liberty Bay without a permit.
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4. Estimates of the impact of continuous and intermittent
bypasses of untreated metal plating waste from the Navy Torpedo
Station to Liberty Bay indicated these sources would produce some
increase in the seawater concentrations of cadmium, chromium, and
nickel. However, resulting metal levels at the Sea Farms hatchery
site would not have exceeded concentrations suggested by the National
Academy of Sciences (1972) as being hazardous in the marine environ-
ment. The combined contribution of bypasses of these and other
metals by the Torpedo Station was also estimated not to have exceeded
a hazardous level at the Sea Farms site.
5. The relative toxicity to oyster embryos of treated effluents
from local sewage treatment plants followed the order: Poulsbo > Navy
Torpedo Station > Keyport. Dilution simulations indicated that under
certain conditions treated effluent from the Poulsbo plant may have
been toxic to oyster embryos and larvae when it reached the Sea Farms
hatchery site.
6. Most Liberty Bay waters and sediments collected during the
survey were not acutely toxic to Pacific oyster embryos during 48 hour
exposure periods. The larval mortalities and abnormalities that were
observed in certain seawater samples were associated with an algal
bloom occurring In the east—central portion of the Bay. The bloom
was composed primarily of the dinoflagellates, Gyninodinium splendens
and Prorocentrum gracile . Although related algae have been implicated
in past mortalities of marine organisms, it was not known if these
species were directly responsible for the toxic effects observed or
If bacterial and fungal metabolites were involved.
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7. Sediment toxicities appeared to be more closely related to
total volatile solids concentrations in the sediments than to metal
or sulfide levels. Although this observation suggested that certain
organic constituents in the sediments were adversely affecting oyster
embryos, its significance was not entirely understood.
8. The cause of the oyster embryo and larval mortalities expe-
rienced by Sea Farms, Inc. could not be determined. A few factors
were identified, however, that probably contributed to the mortality
problem, particularly when present in some combination with each
other over an extended period. These factors included:
1. toxic metabolites of algal, bacterial, or fungal origin,
2. infectious diseases,
3. treated effluent from the Poulsbo sewage treatment plant,
and
4. suspensions of sediments containing relatively high
concentrations of metals, suif ides, volatile solids,
and Pearl Benson Index (PBI)—sensitive substances.
Bypasses of metal plating wastes and other discharges from the
Navy Torpedo Station were estimated not to have seriously impacted
Liberty Bay water quality in the vicinity of the Sea Farms hatchery.
It cannot be definitely stated, however, that past discharges of
unknown volume and character would not have been toxic.
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(Recommendations)
1. The conditions responsible for violations of the Federal Water
Pollution Control Act and the National Pollution Elimination System that
resulted in unpermitted discharges of metal plating waste, domestic
sewage, and heated seawater to Liberty Bay should be corrected imme-
diately. Certain corrective action has already been taken. Follow—up
inspections should be conducted to assure that permanent elimination
of these violations has been achieved.
2. The sewage treatment facilities of the City of Poulsbo should
be improved to provide at least secondary waste treatment, with the out-
fall being located outside the Liberty Bay system.
3. Develop a program, in cooperation with other agencies, to
chemically and biologically monitor water, sediments, and shellfish
from selected stations in Liberty Bay, other Puget Sound areas, and
the coastal zone. The primary purpose of such an effort would be to
provide for the timely detection of environmental quality problems as
well as improvements in quality associated with improved waste treat-
ment practices.
4. Aquaculture activities, including oyster hatcheries, should
only be located in areas having year—round supplies of high quality
water. Site selection should be preceded by a comprehensive chemical
and biological water quality evaluation to assure that this requirement
is met.
5. The effects of selected algal, bacterial, and fungal inetabo—
lites on the development and survival of Pacific oyster embryos and
larvae should be investigated.
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6. Determine in more detail the factors affecting phytoplankton
production in Liberty Bay, with emphasis on the possible stimulatory
or inhibitory effects of sewage treatment plant discharges and metal
plating wastes.
7. The individual and combined effects of metals and other poten-
tial toxicants on the development, survival, and growth of Pacific oyster
embryos, larvae, and juveniles should be determined using long—term as
well as short—term bioassays.
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DESCRIPTION OF STUDY AREA
Location and General Use
Liberty Bay is one of several small bays comprising the west—
central Puget Sound basin (Fig. 1). Although houses dot much of
the Bay’s shoreline, the major population centers bordering the Bay
include Poulsbo in the northeast and the Navy’s Keyport Torpedo Sta-
tion in the southwest (Fig. 2). Marine waters in the area are used
primarily for navigation, aesthetic enjoyment, recreation, shellfish
culture, and the dilution of wastes.
y rography and Circulation
The Bay is part of the relatively shallow Port Orchard oceano-
graphic system (Fig. 2) located west of Bainbridge Island and joined
to the main Puget Sound basin by Agate Passage and Port Madison to the
north and by Rich Passage to the southeast. Water depths and basin
configuration determine the water circulation characteristics within
the system. Although circulation Is primarily tide—driven, it can be
markedly influenced by wind in some locations. A narrow “S”—shaped
channel formed by the Keyport and Lemolo peninsulas joins Liberty Bay
with the north Port Orchard basin. The maximum depth of this channel
is about 40 feet. Although the Bay proper has a small central basin
with a maximum depth of 52 feet, depths throughout much of the northern
and western portions of the bay are 15 feet or less, with mud flats
being exposed during low tide (Lincoln and Collias, 1975).
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VANCOUVER ISLAND
CANADA
MISERY POINT
REFERENCE STATION
HOOD
CLAM BAY
REFERENCE STATION
TACOMA
Figure 1. Location of Liberty Bay and survey reference stations.
WASHINGTON
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SCALE IN YARDS
E 1
POPULATED AREAS
VERDALE
BURKE BAY
UNIVERSITY
ISLAND
PORT MADISON
HARBOR
Figure 2. Port Orchard oceanographic system.
HARBOR
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Most of the water involved In the flushing of Liberty Bay enters
and leaves via Agate Passage (U.S. Dept. of Commerce, Tidal Current
Charts; Lincoln and Collias, 1975). During drogue studies conducted
by Roats Engineering (1970), water leaving Liberty Bay under conditions
of maximum ebb tide reached a point just southwest of Point Bolin,
then reversed direction after traveling a short distance to the north-
west as flood tide began (Fig. 3). Water entering the Bay under maximum
flood tide conditions tended to flow slightly east of the long axis of
the Bay, reversing direction in a counterclockwise fashion off Poulsbo
prior to ebb tide.
Sediments
Sediments within Liberty Bay show a distinct Increase in their
muda content as the head of the Bay is approached (Fig. 4). Sediments
in the narrow channel connecting Liberty Bay with the north Port Orchard
basin have the lowest mud content (5—10%), while sediments in the deep
basin north of Virginia Point and adjacent to Poulsbo exhibit the
highest percentage mud (80—90%) (Harmon, Serwold, and Marine Science
Technicians, 1976). These sediment characteristics appear to be strongly
influenced by tidal velocities and current patterns, and are considered
to be a major factor influencing the distribution of metals in surface
sediments within the Liberty Bay system.
aGeneral classification of particles <1/16 mm in size using Wentworth
scale.
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1200 2400 1200
24 hour time basis
TIDAL STAGE
DEC.18 - DEC.19 1964
HATCHERY
200 2400 1200
24 hour time basis
TIDAL STAGE
N
1500 3000
Scat, in F. ,t
PATH AND DIRECTION OF CURRENT
DRAG
2230 TIME
VELOCITY IN FEET PER MINUTE
Figure 3. Currents within the Liberty Bay system during maximum ebb and flood tides.
(After Roats Engineering, 1970)
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Scandi
0 500 000
ii
o ,o
o 0
c, o o•
03
PERCENT MUD
90
80
60
40
20
10
6
0
HAIC HE RY
SCALE IN YARDS
Figure 4. Surface sediment characteristics within the Liberty Bay system.
(After Harmon et al., 1976)
13
POULSBO
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Fisheries Resources
Liberty Bay and Dogfish Creek support a variety of organisms of
ecologic and economic importance. Adult chinook, coho, and chum salmon
( Oncorhynchus tshawytscha , 0. kisutch , and 0. keta ) enter Dogfish Creek
to spawn, while the Bay provides a temporary habitat for juvenile coho
and chum salmon migrating from other streams in Puget Sound. The
Bay’s intertidal beaches are important spawning grounds for surf smelt,
Hypomesus pretiosus . In addition to supporting populations of young
smelt, Liberty Bay serves as a nursery ground for important forage
fishes such as herring, Clupea pallasii , and the Pacific sand lance,
Ammodytes hexapterus (Personal Communication, Earl Finn, Washington
State Dept. of Fisheries; Millikan, Penttila, and Day, 1974).
Large numbers of native littleneck clams, Venerupis staminea ,
Japanese littleneck clams, V. japonica , and butter clams, Saxidomus
ganteus , inhabit many of the Bay’s sand—gravel—cobble beaches. Of
major economic Importance to the area is the commercial cultivation
of Pacific oysters. The average value of Pacific oysters landed in
the vicinity of Poulsbo from 1972—1974 was $113,576 (Kitsap County
Planning Department, 1973). Two sections of the Bay have been spe-
cifically classified as “conditionally approved” for the commercial
harvesting of oysters and clams. The approved status of these areas
Is contingent on the proper operation of the sewage treatment plants
discharging to the Liberty Bay system (Personal Communication, Max Hays,
Washington State Department Social and Health Services).
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Water Characteristics
Liberty Bay waters are classified as AA (Extraordinary) by the
Washington State Department of Ecology. The DOE standards on which
this classification is based appear in Appendix A.
Complete water quality data on Liberty Bay are limited. The
information presented below is based on a recent oceanographic study
of the Port Orchard system conducted during the spring and summer
of 1975 by Lincoln and Collias (1975). The study was initiated to
provide information for use in selecting marine sites for the future
discharge of treated wastes from the K.itsap peninsula.
Temperature —
Spring water temperatures In Liberty Bay generally ranged from
9 C to 10 C throughout the water column, with temperatures increasing
slightly toward the head of the Bay. By early August surface temp-
eratures were as high as 17 C in certain locations, and a vertical
temperature gradient had become established in the lower Bay.
Liberty Bay waters were generally 2 C warmer than other waters
of the Port Orchard system. This characteristic was attributed to
the warming effect of the mud flats at the head of the Bay coupled,
of course, with the overall influence of solar radiation.
Salinity —
Salinities throughout Liberty Bay generally ranged from 28 —
29.5 0/00, with the greatest dilution confined to the head of the Bay
where Dogfish Creek enters the system.
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Nutrients —
Waters entering Liberty Bay from Port Orchard contained sufficient
quantities of inorganic phosphate, silicate, and nitrate to support a
substantial spring bloom of phytoplankton. Nutrient reductions asso-
ciated with increases in phytoplankton production suggested that sili-
cate and nitrate were the limiting nutrients in the Port Orchard system.
The productivity of waters at a representative station off Battle
Point (Fig. 2) ranged from a low of about 10 ing—C/m 3 /O.5 day in April
to a high of 742 mg—C/m 3 /O.5 day measured during the phytoplankton
bloom in May. Companion chlorophyll—a values ranged from an April
low of <2 mg/rn 3 to a May high of 20 mg/rn 3 in the upper 6 meters.
Dissolved Oxygen —
Dissolved oxygen concentrations in Liberty Bay usually ranged
from about 7.5 — 9.5 mg/l throughout the water column and were never
observed to be less than 6.9 mg/l. In the spring, concentrations as
high as 14 mg/i (160% saturation) were measured in the surface
waters of the upper Bay. These elevated concentrations resulted from
increased primary production associated with the spring phytoplankton
bloom.
Point Source Discharges
The sewage treatment facility of the City of Poulsbo constitutes
the major point source discharge to the Bay. This primary treatment
plant, constructed in 1942, serves a population of about 2000 persons
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and has an average discharge of 0.25 million gallons per day (MCD)
(State of Washington, 1974). Treated wastes are discharged south
of the Poulsbo marina breakwater at a depth of —12 ft (MLLW) (Fig. 5)
(Personal communication, Herb Armstrong, City Engineer, Poulsbo, WA).
The Poulsbo plant has not yet been issued an NPDES permit. Planning
for the construction of larger and more effective treatment facilities
was initiated by the City a number of years ago. Decisions concerning
these plans are pending.
Major point source discharges to waters adjacent to Liberty Bay
include the waste treatment facilities of the City of Keyport (NPDES
Permit WA—002445—7) and the Navy Keyport Torpedo Station (NPDES Permit
WA—002198—9). These facilities are located along the northern shore
of the Keyport peninsula and discharge treated wastes at depth into the
channel connecting Liberty Bay with the north Port Orchard basin (Fig. 5).
Keyport’s extended aeration plant was constructed in 1968 and has an
average discharge of 0.055 MGD.
The Torpedo Station operates an activated sludge sewage treatment
plant having an average discharge of 0.088 MCD in 1975. In addition to
handling sanitary wastes, this facility presently receives pretreated
discharges from the Station’s electroplating plant. The plating plant
operates on an 8 hour day with a discharge of 0.014 MGD or less. From
about 1936 to February 24, 1975, however, all metallic electroplating
wastes were discharged without treatment at or near the surface of the
channel near Liberty Bay. The discharge site was located southeast of
the present Navy STP outfall (Fig. 5). After this date, when flows of
untreated electroplating wastes occasionally exceeded the approximate
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STORM SEWER
D Sc HAR GE
WASTE TREATMENT
FACILITIES
A DISCHARGE POINT
POPULATED AREAS
SCALE IN YARDS
HATCHERY
Figure 5. Location of waste treatment facilities and major discharge points within
the Liberty Bay system.
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30 gallon per minute (GPM) capacity of the pretreatment facility, or
when the STP was not operating properly, the excess untreated plating
wastes were discharged to the channel southeast of Liberty Bay through
the original outfall (Personal Communication, Dick Boughner, U.S. Navy,
Seattle, WA). Such discharges were not permitted under the National
Pollutant Discharge Elimination System (NPDES) permit applying to the
Torpedo Station STP. This situation has since been corrected resulting
in the overflow outfall being sealed shut in November, 1975.
The volume and nature of the plating wastes have remained about
the same over the last few years. The discharge capacity of the
plating plant will be increased, however, when improvements currently
being made in the pretreatment facilities are completed later this
year (Personal Communication, Dick Boughner, U.S. Navy, Seattle, WA).
Minor point source discharges to the Liberty Bay system include
oyster washings from Coast Oyster Company (NPDES Permit WA—000116—3)
as well as the drainage from numerous storm sewer outfalls. In addition
to these sources, the discharge of heated seawater from the Sea Farms
oyster hatchery constituted an unpermitted thermal discharge to the
upper Bay before the hatchery discontinued its operation.
Nonpoint Source Discharges and Other Activities
A small landfill located in the southwestern sector of the Navy
Torpedo Station constituted a potential nonpoint source discharge to
the Liberty Bay system. Limited quantities of assorted refuse were
discarded at the site until it was closed in 1975. Reports that
19
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mercury—cadmium batteries had in the past been disposed of in the
vicinity of the landfill could not be confirmed (Personal Communica-
tion, Dick Boughner, U.S. Navy, Sand Point, WA).
Another activity of potential significance that was considered
during the survey included past experimental applications of various
toxicants to small areas of Liberty Bay f or the control of Japanese
oyster drills, Ocinebra japonica . Field evaluations of such agents
as mercuric chloride, copper sulfate, cuprous chloride, cupric chloride,
and lead nitrate were conducted during the late 1940’s and early 1950’s,
with orthodichlorobenzene and Sevin being applied on a small scale in
1960 (Bajkov, 1949; Fullington and Woelke, 1951—1953; Lindsay, 1961).
The grouting of several sewer lines serving the Poulsbo STP was
also considered. Grouting activities were only conducted, however,
between August 1, 1975 and October 12, 1975. The grout used was an
acrylamide gel (Cyanamid A1 -9) that did not contain mercury (Personal
Communication, Gel—Co Grouting Surface, Salem, OR, and American
Cyanamid Co., Wayne, NJ).
20
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METHODS
Field Activities
Sampling —
Sampling of Liberty Bay and reference stations established in
Hood Canal (Misery Point) and Clam Bay (Manchester) (Figs. 1 and 6)
was conducted September 12 — 19, 1975. Water, sediment, fish and
shellfish samples were collected during this period. Additional
water samples were collected in October, November and December, 1975
to continue to provide water quality surveillance as well as to help
answer questions raised about the goodness of the analytical techniques
being used.
Specific details concerning the collection and storage of each
type of sample are presented below.
Water
Water samples were collected with a polyvinyl chloride (PVC)
Van Dorn bottle or Kemmerer sampler, then poured into 1—liter, poly-
ethylene Cubitainers for chemical analysis or into clean, 4—liter
polypropylene jugs for bioassay. On occasion, surface samples were
collected directly in the Cubitainers or polypropylene jugs. Samples
collected for chemical analysis were stabilized in accordance with
the EPA Manual of Methods for Chemical Analysis of Water and Wastes
(1974) depending on the chemical parameter of interest. All water
samples were placed in ice chests for transport to the laboratory.
Chemical analysis of the samples was initiated immediately, or as
21
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W WATER
S - SURFACE SEDIMENTS
F FISH
St SHELLFISH
C BOTTOM CORE
0 500
SCAt tN YARDS
—WSF -3
REFERENCE STATIONS
HOOD CANAL ( MISERY PT,) - WSFSF
CLAM BAY WSFSF
R HATCHERY
WSF -5
S114
/
/
,
/
Figure 6. Location of sampling stations.
SYMBOLS
N
22
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soon as possible, upon their receipt by the laboratory. Bioassay
samples were refrigerated at 1 C for approximately 24 hours before
being prepared for toxicity assessment. One 4—liter sample of Clam
Bay water was collected the morning of September 15 and carried along
during the sampling tour. This sample served as the “carry along
control” to detect changes in water quality associated with the col-
lection, transport, and storage of the bioassay samples.
During the period of most intensive sampling (September 15),
water samples were collected from five Liberty Bay stations at the
surface, mid—depth, and bottom during low slack and high slack tides.
Samples collected from Hood Canal and Clam Bay (September 17) were
collected only at the surface and bottom under conditions of low and
high tide respectively. All other water samples could be character-
ized as surface grabs collected only for chemical analysis under a
variety of tidal conditions.
Sediment
Surface sediments were collected with a Van Veen grab or by
hand at eighteen Liberty Bay stations (Fig. 6) and at the two ref er—
ence stations. Sediment was transferred to, or was collected in,
new glass jars and stored at about 4 C until analyzed or bloassayed.
Duplicate sediment core samples were collected from each of six
Liberty Bay stations (Fig. 6) with a Phieger corer equipped with new
plastic core liners. The cores were refrigerated immediately after
being collected. Later, they were frozen in their liners to facil-
itate the removal of top and middle sections for chemical analysis.
23
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The bottom portion of each core was retained by the corer bit.
These sections were placed in glass jars and analyzed as soon as
possible after collection.
Fish
Bottom fishes were collected with a spear gun by SCUBA divers
from five subtidal stations in Liberty Bay and from the two survey
reference stations (Fig. 6). The fishes were later frozen in plastic
bags. Prior to chemical analysis the samples were thawed, measured,
and filleted. The muscle tissue fillets from each fish were placed
in glass jars and kept refrigerated (4 C) until analyzed.
Shellfish
Several species of shellfish were collected by hand during low
tide at ten intertidal stations in Liberty Bay (Fig. 6) as well as
from the Hood Canal and Clam Bay reference stations. Samples of
oysters, butter clams, and littleneck clams, each consisting of about
six, twelve, and twenty—four specimens respectively, were placed in
plastic bags and frozen in the shell before being shucked. Drained
shellfish meats were stored in glass jars at 4 C.
Hydrographic Measurements —
During periods of intensive water sampling, several hydrographic
parameters were measured in situ at each sampling site by the use of
a portable water quality monitor (Hydrolab Surveyor 6—D). These para—
meters included water temperature, dissolved oxygen, pH, and depth.
The instrument was calibrated prior to each sampling tour.
24
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Laboratory Activities
Chemical —
The need for descriptive information on the chemical character
of Liberty Bay required that a variety of chemical and physical
parameters be measured in the water, sediment, and biological samples
collected during the survey. These measurements were performed
according to the methods listed in Table 1.
The accuracy (recovery efficiency) of major chemical analyses
performed on samples collected during the survey was determined by
the standard additions technique (U.S. EPA, APTD—l132, 1973). Stan-
dard reference samples used for this purpose were obtained from the
EPA Environmental Monitoring and Support Laboratory, Cincinnati,
Ohio.
Biological —
Oyster Embryo Bioassay
Selected seawater, sediment, and sewage treatment plant (STP)
effluent samples were assayed September 16 using modifications of
the general Pacific oyster embryo assay technique of Woelke (1972).
The actual procedures followed during each step of the assay are
described below.
Sample Preparation
( Water ) l000—ml volumes of sample were poured into each of
two 1—liter polyethylene beakers.
25
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Table 1. Analytical Methods Followed During Survey of Liberty Bay.
Parameter Sample Type Analytical Method Reference
Metals (Total)
Sb, As, Cd, Cr, Cu, Fe, Pb, FW U.S. EPA — Methods for Chemical Analysis,
Mn, Ni, Be, Zn 1974.
SW Lakanen, 1966. Perkin-Elmer Instrument
Manual, 1973; U. S. EPA, Methods for
Chemical Analysis, 1974.
Sd Perkin-Elmer Instrument Manual, 1973;
Sh U. S. EPA — Methods for Chemical Analysis,
1974, Lakanen, 1966.
Hg FW, SW, Sd, Sh U. S. EPA Methods for Chemical Analysis,
1974.
Cr (Hexavalent) FW, SW APH.A - Standard Methods, 1972.
Organochlorine Compounds Sd, Sh U. S. EPA - Analysis of Pesticide
Residues, 1974.
Nutrients
Total Phosphorus; NH 3 -.N FW, SW U. S. EPA — Methods for Chemical Analysis,
1974.
Miscellaneous
TOC; BOD; MBAS; Cyanide; FW, SW U. S. EPA - Methods for Chemical Analysis,
Turbidity; N-Kjeldahl; Sd 1974.
Total Volatile Solids; Total
Solids
Total Sulfide FW, SW, Sd APHA - Standard Methods, 1972.
PBI (Pearl-Benson Index) FW, SW Barnes, C.A. at al.,1963.
Salinity Sw Zerbe and Taylor, 1953.
FW Freshwater
SW Seawater
Sd Sediment
Sb Fish and Shellfish
26
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Ten 1—liter volumes of Clam Bay seawater collected during the
sample preparation activities served as the “bioassay control.”
( Sediment ) 10, 1, 0.1, and 0.01 grams of sediment were weighed
separately into each of two 1—liter polyethylene beakers. The contents
of the beakers were then brought up to 1000 ml with Clam Bay, bioassay
control, seawater.
( STP Effluent ) Serial dilutions of treated effluent were
made based on a dilution factor of 2.0. Each dilution was prepared
by adding appropriate volumes of effluent to each of two 1—liter
polyethylene beakers, then bringing the contents up to 1000 ml with
Clam Bay, bioassay control, seawater. Care was taken to maintain the
salinity of the final effluent preparations above 24 o/oo. Salini—
ties <20 o/oo have been found to adversely affect oyster embryo
development (Woelke, 1972).
Oyster Spawning and Sample Inoculation
Spawning was induced in adult Pacific oysters harvested from
Burley Lagoon (Western Oyster Co.) and conditioned at approximately
19 C for three weeks. Eggs were fertilized with a sperm suspension
obtained by spawning, and each 1—liter sample preparation was inocu-
lated with 3.0 x l0 developing embryos approximately two hours after
fertilization. The cultures were covered with brown paper and air—
incubated for 48 hours at 20 C.
Salinity and pH measurements were made on selected sample prep-
arations at the end of the 48—hour incubation period.
27
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Termination
Sediment assays were terminated by carefully vacuuming the
larval culture into a flask without disturbing the settled sediment.
The culture was then mixed with a magnetic stirrer and 10 milliliters
transferred to a screw—cap vial and preserved in 5% formalin. All
other assays were terminated as described above, but without the
Initial vacuum transfer step. This procedure was used to prevent
the mechanical loss of larvae using the filter termination technique
as shown to be possible by Cardwell et al., (In preparation).
Larval Enumeration
The fluid overlying the preserved larvae was removed with suction
and the larvae quantitatively transferred to a Sedgwick—Rafter cell.
The normal and abnormal larvae were counted under a microscope at
100 X. Those embryos failing to develop to fully—shelled, straight
hinge larvae were considered to be abnormal.
Bioassay Evaluation
Evaluation of oyster embryo response to the various sample prep-
arations was based on larval development and survival using measurements
of per cent larval abnormality and per cent relative larval survival.
Per Cent Larval Abnormality : The proportion of abnormal
larvae to the total number of larvae (normal and abnormal)
in a sample.
Per Cent Relative Larval Survival : The proportion of the
total number of larvae (normal and abnormal) in a sample to
the mean total number of larvae (normal and abnormal) in
the “bioassay control” sample.
28
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Plankton Identification and Enumeration
The major phytoplanktonic and protozoan species present in selected
water samples from Liberty Bay were identified by personnel of EPA ’s
Narragansett Environmental Research Laboratory, Narragansett, Rhode
Island.
Phytoplankton population densities were determined by the use of
a hemacytometer.
Compliance Monitoring Inspection
An independent compliance monitoring inspection of the Navy
Torpedo Station STP was conducted by EPA in conjunction with the
chemical and biological survey of Liberty Bay. The primary purpose
of the inspection was to assess compliance with the National Pollu-
tion Discharge Elimination System (NPDES) permit conditions. This
activity, coupled with effluent sampling of the Poulsbo and Keyport
STPs, also provided needed information on the characteristics of the
major point source discharges to the Bay. The field and laboratory
methods that were applied were generally the same as those described
earlier.
29
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RESULTS AND DISCUSSION
Chemical and Physical Characteristics
Water —
General Conditions
The basic chemical and physical properties of selected Liberty
Bay, Clam Bay and Hood Canal waters during the period September 15 —
October 10, 1976 are presented in Table 2.
Liberty Bay water temperatures generally decreased with depth
and toward Dogfish Creek. Bottom water temperatures ranged from 13.5 —
16.0 C, while surface waters in the central and lower Liberty Bay sys-
tem ranged from 16.0 — 17.0 C. Salinity and pH values showed little
variation, ranging from 29.4 — 30.4 o/oo and 7.2 to 8.0, respectively.
Turbidities usually ranged from 0.8 — 7.5 nephelometric turbidity units
(NTU), with a high value of 27 NTh characterizing the bottom water at
Station WSF—5 (Sea Farms hatchery site).
Dissolved oxygen concentrations (DO) in the Bay’s surface waters
ranged from 9.1 — 12.5 mg/l, while the overall range of DO levels in
waters collected at middepth and near the bottom ranged from 4.8 — 8.5
mg/i. Similarly, surface total organic carbon (TOC) values ranged
from 2.0 mg/i to as high as 50 mg/i, with middepth and bottom values
ranging from 2.0 — 3.0 mg/i. The higher p11, DO, and TOC characteristics
of the surface waters undoubtedly reflected the influence of increased
phytoplankton growth in the Bay’s surface waters. A phytoplankton bloom
observed in east—central Liberty Bay on September 15 was evidence of
30
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Table 2. General
Physical and Chemical
Properties
of Liberty Bay,
Clam Bay,
and Hood Canal Waters.
Station
Dete
Time
Tidal
Stage
Sep-tb
(in)
Temperature
(C)
Salinity Turbidity
°/oo pH NTU
Dissolved
Orygen (mg/i)
PBI’°
(Tag/i)
N—NH 3
(mg/i)
Total
Pboophorus (mg/i)
Total Organic
Carbon (mg/i)
Sulfide
(mg/i)
Cyanide
(mg/i)
NHAS
(mg/i)
Liberty Bay Stations
WS—0 10—7-75
(Segfish Creek)
1215
mw-Ebb
0
10.1
1.3
5.0
0.02
0.043
*SF—3 9-15-75
(Near Poulmbo STP Outfall)
1630
High-Slack
0
5
9
14.9
14.0
13.5
30.4
29.5
29.7
8.0
7.6
7.2
2.6
1.5
1.8
12.5
8.5
4.8
<1.0
2.0
<1.0
0.03
0.05
0.07
0.28
16.0
3.0
3.0
<0.02
00.02
<0.02
1.01
0.100
0.045
0.045
F—3 9-15-75
1055
Low-Flood
0
3
6
14.0
13.8
13.5
29.5
29.4
29.7
7.7
7.4
7.5
1.6
1.4
4.1
9.1
7.0
6.5
2.0
3.0
<1.0
0.12
0.04
0.03
0.20
9.0
2.0
3.0
<0.02
<0.02
<0.02
<0.01
0.055
0.030
0.023
WSF-5 9-15—75
(Oyster Hatchery Site)
1610
High-Slack
0
5
9
15.0
14.6
14.0
29.5
29.5
29.7
7.8
7.6
7.5
2.8
1.2
27
12.0
8.3
7.8
1.0
1.0
9.0
0.03
0.04
0.06
0.22
17.0
2.0
2.0
<0.02
<0.02
<0.02
<0.01
0.090
0.013
0.020
WSF—5 9—15—75
1015
Low-Flood
0
3
6
14.5
14.0
14.0
29.6
29.7
29.7
7.7
7.5
7.5
1.2
1,2
2.8
10.0
7.8
7.3
3.0
1.0
<1.0
0.04
0.03
0.04
0.10
4.0
3,0
3.0
<0.02
<0.02
<0.02
<0,01
0.050
0.018
0.010
WS—7 9-15—75
(Mid—Bay)
0940
Low-Flood
0
3
6
17.0
13.5
13.5
29.4
29.7
29.9
7.7
7.5
7.5
7.5
1.7
2.4
10.5
7.2
6.8
3.0
3.0
1.0
0.07
0.04
0.05
0.55
0.09
0.10
50.0
3.0
3.0
<0.02
<0.02
<0.02
<0.01
0.440
0.013
0.013
W-li 9—15—75
(1 uth of Bay)
1545
High—Slack
0
6
12
16.0
15,0
13.5
29.7
29.8
29.9
7.7
7.6
7.5
1.2
1.3
1.0
11.0
8.0
7.1
1.0
1,0
3.0
0.02
0,03
0.04
0.11
4,0
2.0
2,0
<0.02
<0,02
<0.02
<0.01
0.055
0.020
0.013
W-1l 9—15—75
09(82
Low—Slack
0
5
9
16.5
16.5
16.0
29.8
29.5
29.5
7.7
7,7
7.6
0.9
1.2
2.3
10.0
8.1
7.1
1.0
1.0
2.0
0.02
0.04
0.04
0.08
2.0
3.0
3.0
<0.02
<0.02
<0.02
<0.01
0.045
0.015
0.010
WSF—13 9—15—75
(Keyport STP Outfall)
0800
Low—Slack
0
6
12
17.0
17.0
14.7
29.8
29.8
29,9
7.7
7,7
7.6
1.1
1.0
0.8
11.9
7.8
7.2
<1.0
<1.0
1.0
0.03
0.03
0.03
0.82
3,0
3.0
3.0
<0.02
<0.02
<0.02
<0.01
0.045
0.020
0.010
Y -l7 9—17—75
(NTSb Paint Shop Storm
Sewer Outfall)
1230
Low—Flood
0
WSF—19 9-17—75
(Near NTS Plating Plant
Overflow)
1200
Low—Flood
1
0.04
2.0
<0.01
WS—22 9—17—75
(NTS S,E. Lagoon)
0900
Low—Ebb
0
5.8
3.9
5.0
0.05
9.0
<0.01
WS—23 10—10—75
(NTS N.W. Lagoon)
1215
High—Ebb
0
2.7
<1.0
0.09
Reference Stations
Hood Canal (Misery Pt.) 9—16—75
1110
Low—Flood
0
8
15.6
11.5
24.2
29.3
7.9
7.5
0.5
1.6
11.8
7.7
2.0
2.0
0.02
0.02
0.032
3.0
3.0
<0.02
<0.02
<0.01
Clam Bay 9-16—75
-
1355
Low—Flood
0
11
11.9
11.2
29.8
29.9
7.6
7.6
0.5
0.6
8.1
8.1
1.0
1.0
0.03
0.04
0.074
2.0
2.0
<0.02
<0.02
<0.01
aN7 J Nephelometric turbidity units
bpBI Pearl-Benson Index
CNTS Navy Torpedo Station
‘ MBAS Uethylene Blue Active Substances
-------
such increased primary productivity. The species composition and pos—
sible significance of the bloom are discussed in more detail in the
Biological section of this report.
Ammonia—nitrogen (N—NH 3 ) levels generally ranged from 0.02 — 0.07
mg/i, with the highest value of 0.12 mg/i being measured at the surface
near the Poulsbo STP outfall during low tide. These values were similar
to the levels measured in Liberty Bay by Lincoln and Collias (1975); how—
ever, the vertical and horizontal concentration gradient they observed
earlier was not as apparent in September.
Total phosphorus concentrations in the Bay’s surface waters (0.098
— 0.55 mg/i) were consistently higher than those at the surface of the
channel leading from the Bay (0.080 — 0.082 mg/i). There appeared to
be a direct relationship between these concentrations and TOC values
throughout the system. This relationship probably reflected increases
in the concentrations of cell—associated phosphorus linked to substan-
tial increases in the standing crop of phytoplankton.
Sulfide levels measured throughout the water column were below
detectable limits (<0.020 mg/i). The indeterminately low nature of
these values precluded the assessment of their biological significance
based on sulfide concentrations (>0.01 mg/i) suggested as hazardous by
the National Academy of Sciences (1972). Both the indeterminate levels
and the suggested hazardous concentrations were considerably lower,
however, than the 0.2 mg/i sulfide levels reported by Sea Farms, Inc.
in surface waters near the oyster hatchery April 28, 1975 (Personal
Communication, Sea Farms, Inc. Pouisbo, WA). The only known activity
that may have been responsible for the high sulfide concentrations
32
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reported by Sea Farms was a bottom dredging operation that was con-
ducted just north of the Poulsbo marina from April 2—21, 1975 (Per-
sonal Communication, Herb Armstrong, Roats Engineering, Poulsbo,
Washington). Dredged material removed from the Bay was used to
backfill a shoreline bulkhead near the dredge site. Consequently,
the settling and draining of this material may have had a limited
effect on the Bay’s water quality for some time following the coinpie—
tion of dredging. Although it was possible that the dredge and spoil
disposal operation resulted in an increase in seawater — sulfide
concentrations to harmful levels, no positive correlation between
the total sulfide content of Liberty Bay sediments and acute oyster
embryo response could be demonstrated in the laboratory (page 103).
The concentrations of Pearl—Benson Index (PBI)—sensjtive sub—
stancesa generally ranged from 1.0 — 3.0 mg/i; however, an unexplained
high value of 9.0 mg/i characterized bottom waters at the Sea Farms
hatchery site (Station WSF—5). The unusually high turbidity of this
water (27 NTU) suggested that a small amount of bottom sediment may
have been inadvertently collected along with the sample of bottom
water. If a portion of this bottom material were PBI—sensltive, it
could explain the 9.0 mg/i PBI measurement. Based on the reports of
Gunter and McBee (1960) and Woelke (1960), the 9 mg/i PBI value
approached or slightly exceeded the levels of sulfite waste liquor
(as measured by the Pearl—Benson method) found to affect Pacific
oyster development. No discharges of sulfite waste liquor are known
aSubstances responding positively to the Pearl—Benson method of esti—
mating sulfite waste liquor concentrations in water.
33
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to have been made to Liberty Bay. Therefore, the PBI—sensitive sub-
stances in the Bay probably consisted primarily of naturally occurring
tannins and lignins. Although of possible biological significance,
the effect of such substances on oyster embryo development and sur-
vival has not been well defined. The levels of PBI—sensitive sub-
stances measured in Liberty Bay waters did not, however, appear to
adversely affect embryo response during the acute oyster embryo assays
performed on these waters (page 91).
Cyanide concentrations ranged from <0.01 mg/i to a determinate
level of 0.01 mg/i at Station WSF—3 near the Poulsbo STP outfall.
Although the 0.01 mg/i value equaled the hazardous level (>0.01 mg/i)
suggested by the National Academy of Sciences (1972), this measurement
represented the lower limit of detectability and, therefore, should be
confirmed before assessing its possible biological significance.
Concentrations of methylene blue active substances (MBAS) in
Liberty Bay ranged from 0.10 — 0.440 mg/i, with distinctly higher
levels being observed in surface waters. The measurement of MBAS is
commonly used to indirectly determine the concentration of linear
alkylate sulfonate (LAS) surfactants. These substances (LAS) are cur-
rently used in household detergents and are considered to be hazardous
to freshwater organisms at concentrations exceeding 0.2 mg/i (National
Academy of Sciences, 1972). Although the Poulsbo STP was shown to be
a major contributor of MBAS to the Bay (Appendix B), the direct
relationship between the MBAS and TOC levels measured in the Bay
suggested that the elevated MBAS levels in the Bay resulted from
the interference of chlorophyll and other pigments associated with
34
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the algal bloom observed during the survey. It was not possible,
therefore, to assign any biological significance to these inflated
MBAS values.
Metal Concentrations
Most of the total metal levels measured in Liberty Bay waters
exceeded concentrations reported by the National Academy of Sciences
(1972) as characterizing unpolluted seawater. Levels of cadmium, Iron,
mercury, nickel, and zinc even exceeded concentrations suggested by
the Academy as being hazardous in the marine environment. Signif I—
cantly, most of the metal levels measured at the survey reference
stations in Clam Bay and Hood Canal also appeared to be elevated.
In some cases these concentrations equaled or exceeded metal levels
detected in Liberty Bay.
Before assessing the significance of possible hazardous heavy
metal levels that appeared to be present in Liberty Bay, the extra-
ordinarily high “background” concentrations of metals measured at
the Clam Bay and Hood Canal reference stations had to be explained.
Although the proximity of Clam Bay to industrialized areas of Puget
Sound was considered to lend some credence to the high metal levels
measured there, no such explanation could be offered in the case of
Flood Canal. The need for such an explanation was underscored by the
understanding that Clam Bay and Hood Canal supported healthy biological
communities indicative of good water quality. Furthermore, there were
no apparent geochemical explanations for the high metal concentrations
in the Canal, except perhaps for manganese.
35
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The analytical methods used during the survey have inherent char-
acteristics which would possibly yield total metal concentrations in
seawater that are somewhat higher than levels reported in the litera-
ture. This possibility did not, however, fully explain the magnitude
of the apparent discrepancies. 1etal levels measured by EPA in Hood
Canal. were significantly higher than levels observed in various Puget
Sound and Hood Canal waters by other investigators, regardless of the
techniques used (Chow, 1953; Laevaster, 1954; Tatomer, 1972; Schell
and Barnes, 1974). A laboratory investigation was, therefore, initiated
in an attempt to explain the discrepant results. All procedures were
tested again for repeatability, with reagents and sample containers
also being tested for contamination. The laboratory study revealed
metal contamination of the sample containers, the acid used to pre-
serve the samples, and the filter flasks used to collect filtrates
for dissolved metal analysis. Although the contribution of metal
contaminants from the sample containers and acid was relatively small,
the filter flasks were a source of considerable contamination in
some cases. More importantly, large variations between replicate
analyses were observed which reflected a marked loss of analytical
precision.
The combined evidence is clear. The lack of agreement between
EPA seawater data and that of other investigators; the paradox of
possible toxic conditions in the reference areas with no indication
of biological harm; and the laboratory results showing possible sample
contamination together with a loss of precision led us to discount
36
-------
the seawater metals values. As a result, all EPA seawater metals
data were considered suspect and, with the exception of mercury,
were omitted from the report because of our inability to verify
the accuracy of the findings. In consideration of the intense
interest in the mercury content of Liberty Bay waters, certain
mercury data, corrected for possible laboratory contamination,
were included for discussion.
Metal analyses performed on sediments, fish, and shellfish
were demonstrated to be accurate in addition to yielding results
that were in reasonable agreement with values obtained by other
independent investigators. These data are included in the report
without qualification. Work is continuing in an effort to overcome
the seawater analytical discrepancies encountered during the survey.
(Mercury)
The concentrations of total mercury measured in Liberty Bay,
Hood Canal, and Clam Bay waters during the survey were always <0.7
ugh. Although this indeterminate mercury level represented a lower
limit of detectability that was somewhat higher than the lower limit
(0.2 ug/l) described by the analytical method used (EPA, 1975), it
was considerably lower than the determinate mercury concentrations
(1 — 110 ug/l) reported earlier by Sea Farms, Inc. in Liberty Bay
surface waters.
Sediment —
It was recognized at the outset that the analysis of water samples
alone would probably reveal little in the way of information on past
37
-------
or recently discontinued practices of discharging wastes to the Liberty
Bay system. Sediment samples, and to some extent fish and shellfish,
were collected therefore, for the purpose of providing this historical
information.
Metal Concentrations
( Surface Sediments ) Concentrations of eleven metals measured
in surface sediment grab samples collected during the survey are
listed in Table 3. Metal concentrations measured in surface sediments
at the top of the sediment cores (Table 4) are presented and discussed
with the results of the surface sediment grab sample analyses (Pigs.
7—17).
Metal concentrations in Liberty Bay surface sediments varied con-
siderably, with higher levels generally being measured in the finer—
grained sediments of the central—to—upper Bay. The higher metal content
of these sediments was consistent with the demonstration of Crecelius,
Bothner, and Carpenter (1975) that concentrations of certain elements
(As, Sb, Hg, Fe, and C) in “noncontaminated” Puget Sound surface sediments
tended to increase as the mean grain size of the sediments decreased.
The elevated metal concentrations characterizing sediments behind the
Poulsbo marina breakwater would be expected, therefore, considering the
influence of reduced current velocities in the area on the distribution
and accumulation of finer—grained materials containing or consisting of
metal contaminants as well as “noncontaminated” sediments. The detection
of the highest concentrations of certain metals (Cd, Cr, Pb and Zn) in
the coarser—grained sediments near the Torpedo Station plating plant
overflow outfall and industrial storm sewer system was not surprising,
38
-------
Table 3. Ccncantratlona
of Maca la in Star
face Sedimance fron
Station
Date
Bay
L. Clan Bay and l ined
Concentration
Canal.
Antimony
(Sb)
Arsenic
(As)
Cadmium
ChromIum
yg/g (dry weight)
Copper Iron
Lead
Manganese
Mercury
Nickel
Zinc
Liberty Say Stations
(Cr)
(Cu) (Fe)
(Pb)
(Mn)
(Hg)
(Ni)
(Zn)
wS—o 10-7—75 0.080 6.0 0.60 i6 5.5 12,000 5.6 160 0.030 24 38
(Dogfish Creek)
S—2 9—15—75 0.10 12 4.2 52 39 25,000 25 230 0.14 58 100
(Upper Bay)
WSF—3 9—15—75 0.20 8.0 2.8 33 29 18,000 18 170 0. 1 1 51 65
(Near Poulsbo SIP Outfall)
S—4 9—15—75
-------
however, considering the Navy’s approximate 40—year history of discharg-
ing untreated plating wastes from the Torpedo Station to nearby marine
waters.
Antimony concentrations in Liberty Bay surface sediments usually
ranged from <0.02 — 0.70 ug/g (Fig. 7). These values were generally
considerably lower than the levels (0.3 — 1.0 ug/g) detected in “noncon—
taminated” Puget Sound surface sediments by Crecelius and his associates
(1975).
An average high concentration of 2.6 ug/g was measured behind the
Poulsbo marina breakwater (Station C—F). Although this level was similar
to the concentrations measured at the Clam Bay reference station (3.5
uglg) and at several other central Puget Sound sites, it was well below
levels measured near the Tacoma smelter (Crecelius etal., 1975).
Arsenic concentrations in surface sediments from the Liberty Bay
system ranged from 2.0 — 16 ugfg (Fig. 8). This range was similar to
the range of arsenic levels (3 — 15 ug/g) reported by Crecelius and
co—workers (1975) in “noncontaminated” surface sediments collected from
throughout Puget Sound. It also corresponded to the range reported by
Huntamer and Schell (1974) in surface sediments from Colvos Passage and
Commencement Bay.
Although arsenic levels tended to be higher in those sediments
having a higher mud content, even the higher concentrations were con-
siderably lower than arsenic levels measured by Crecelius and his asso-
ciates (1975) in sediments collected in the vicinity of the Tacoma
smelter. The smelter was considered to be the major man—induced source
of arsenic and antimony to Puget Sound.
40
-------
S ca ndi
0 , 500 000
SCALE IN YARDS
Figure 7. Antimony concentrations in Liberty Bay surface sediments (ug/g dry weight).
REFERENCE STATIONS
HOOD CANAL MISERY PU o.i
CLAM BAY 3.5
LESS THAN <
0 . I
41
-------
SCALE IN YARDS
REFERENCE STATIONS
HOOD CANAL ( MISERY PT.)
CLAM BAY 6.0
Figure 8. ArsenIc concentrations in Liberty Bay surface sediments (ug/g dry weight).
42
-------
Cadmium — Most cadmium levels in Liberty Bay sediments ranged
from 0.70 — 5.1 ug/g, with concentrations within this range being some-
what higher in the upper Bay (Fig. 9). A high concentration of 24 ug/g
was measured in the sediment below the Torpedo Station plating plant
overflow outfall. This observation, coupled with the results of the
Compliance Monitoring Inspection (EPA, 1975), indicated that the
plating plant was at least one maior source of cadmium to the system.
The inspection also showed that relatively small amounts of cadmium
were being added by the poulsbo and Keyport STPs as well as the Torpedo
Station paint shop storm sewer.
An interesting feature characterizing, to varying degrees, the
distribution of cadmium, as well as copper, lead, iron, manganese,
mercury, nickel, zinc, and to some extent chromium, was the relatively
high metal concentration measured at the Sea Farms hatchery site (Sta-
tion WSF—5) compared to most other stations outside the Poulsbo marina
breakwater, including those stations located in proximity of the Torpedo
Station. In the case of cadmium, the 13 ug/g concentration measured
at Station WSF—5 actually exceeded the average concentration (4.3 ug/g)
measured inside the Marina breakwater. In most cases, however, the
metal concentrations detected at the hatchery site were remarkably
similar to those levels measured Inside the breakwater. The reason for
this similarity is not well understood. It suggests, however, that
certain features characteriZing the hatchery site, such as its proximity
to the deep basin to the south, as well as the pier structure and pro-
truding shoreline, may have had an effect on the rate of sedimentation
43
-------
.6
Scandu
0 500 1000
SCALE IN YARDS
Figure 9. Cadmium concentrations in Liberty Bay surface sediments (ug/g dry weight).
111
REFERENCE STATIONS
HOOD CANAL ( MISERY PT. 1.2
CLAM BAY 1.0
44
-------
and particle size distribution that was similar to that of the Poulsbo
marina breakwater. Although the similarity in metal concentrations
at both locations also suggests that the metals came from common
sources, the possibility that different sources were involved cannot
be discounted.
Chromium concentrations ranged from 17 — 180 ug/g, with the dis-
tribution generally following the pattern discussed earlier (Fig. 10).
This range was similar to the range of chromium levels (43 — 199 ug/g)
reported by Crecelius and associates (1975) in surface sediments from
the Puget Sound region.
The highest chromium concentration (180 ug/g) was measured in
surface sediments collected below the Torpedo Station mid—storm sewer
outfall (Station s—18). This concentration, as well as the relatively
high levels of other metals (Cu, Pb, Zn) in the surface sediment below
the mid—storm sewer outfall, was believed to be associated with used
sand—blasting sand that was dumped or washed into the sewer system by
Navy personnel (Personal Communication, Dick Boughner, U.S. Navy,
Seattle, WA).
Copper levels ranged from 7.9 — 70 ug/g in surface sediments
throughout the Liberty Bay system (Fig. 11). The highest concentrations
were measured in the surface sediments behind the Poulsbo marina break-
water (70 ug/g) and at the Sea Farms hatchery site (65 uglg), with
somewhat elevated levels (55 ug/g) detected in the vicinity of the
Torpedo Station. Intermediate Liberty Bay copper concentrations were
generally higher than th levels measured in Colvos Passage sediments
45
-------
500 1000
LJ
SCALE IN YARDS
REFERENCE STATIONS
HOOD CANAL ( MISERY PT) 28
CLAM BAY n
Figure 10. Chromium concentrations in Liberty Bay surface sediments (ug/g dry weight).
46
-------
SCALE IN YARDS
Figure ii. Copper concentrations in Liberty Bay surface sediments (ugfg dry weight).
REFERENCE STATIONS
HOOD CANAL ( MISERY PT ,) 2!
CLAM BAY 2!
HATCAY
0 _ 500 1000
47
-------
by Huritamer and Schell (1974), but were similar to levels found in
Commencement Bay.
The Poulsbo and Torpedo Station sewage treatment plants (STPs)
were contributing forty—eight and forty—nine percent, respectively, of
the copper being added to the system via the three waste treatment
facilities in the area (Appendix B). Other confirmed sources of copper
included the Torpedo Station paint shop storm sewer and plating plant
overflow outfall (EPA, 1975).
Copper lost in the vicinity of the Poulsbo marina in the form of
copper—based bottom paints may be a localized source but quantities
cannot be determined.
Iron — Most iron concentrations ranged from 8 — 32 mg/g, with the
highest level (38 mg/g) being measured behind the Poulsbo marina break-
water (Fig. 12). The lowest concentration (0.20 mg/g) was measured in
the Torpedo Station’s northwest lagoon. The sample on which this low
determination was made was primarily composed of the lagoon’s clay bank
rather than surface sediments, thus possibly explaining the low value
obtained.
The higher concentrations of Iron measured in the Liberty Bay
system were similar to or lower than levels measured by Crecelius and
associates (1975) in surface sediments throughout Puget Sound.
Lead was distributed throughout the Liberty Bay system in a manner
similar to that of the metals already discussed (Fig. 13). Surface sed-
iments at Station S—9 between the Poulsbo STP outfall and the Sea Farms
hatchery site contained only 12 ug/g, while the highest lead level
(190 ug/g) was measured below the Torpedo Station In mid—storm sewer
48
-------
500 1000
SCALE IN YARDS
REFERENCE STATIONS
HOOD CANAL ( MISERY PT) a
CLAM BAY 2
Figure 12. Iron concentrations in Liberty Bay surface sediments (mg/g dry weight).
49
-------
SCALE IN YARDS
REFERENCE STATIONS
HOOD CI NAL ( MISERY PT.) 6.0
CLAM BAY 31
Figure 13, Lead concentrations in Liberty Bay surface sedinients (ug/g dry weight).
50
-------
outfall (Station S—18). Most of the lead concentrations were somewhat
higher than reported by Huntamer and Schell (1974) in sediments from
Colvos Passage, but were similar to levels measured by them In sediment
collected from Commencement Bay.
As mentioned earlier, one source of lead to the Liberty Bay system
was believed to be used sandblasting sand from the Torpedo Station.
Other potentially important sources Included the Poulsbo STP, as well
as the Torpedo Station paint shop storm sewer and plating plant.
Manganese levels ranged from 110 — 410 ug/g throughout the Liberty
Bay system (Fig. 14). Although relatively high manganese concentrations
were measured behind the Poulsbo marina breakwater and at the Sea Farms
hatchery site (300 — 310 ug/g), the highest level (410 ug/g) was found
in the Torpedo Station’s northwest lagoon (Station WS—23). This value
may have been related to the high clay content of the sample collected
at the station rather than to any local source of contamination. The
manganese concentration measured at the Hood Canal (Misery Point) ref er—
ence station (490 ug/g) may also have reflected the influence of local
geologic characteristics. Interestingly, a large number of manganese
deposits exist on the Olympic Peninsula just west of Hood Canal (U.S.
Geological Survey, 1966).
Mercury concentrations In surface sediments throughout the Liberty
Bay system ranged from a low of 0.023 ug/g below the Torpedo Station
plating plant overflow outfall (Station S—20) to a high of 0.37 ug/g
behind the Poulsbo marina breakwater. The concentration of mercury
at the Sea Farms hatchery site (Station WSF—5) was 0.18 ug/g (Pig. 15).
51
-------
500 1Q00
SCALE IN YARDS
REFERENCE STATIONS
HOOD CANAL ( MISERY PT.) 490
CLAM BAY 100
Figure 14. Manganese concentrations in Liberty P’ay surface sediments (ug/g dry weight).
52
-------
SCALE IN YARDS
Figure 15. Mercury concentrations in Liberty Bay surface sediments (ug/g dry weight).
REFERENCE STATIONS
HOOD CANAL ( MISERY PT ) 0026
CLAM BAY 0097
0 500 1000
53
-------
The lower range of mercury levels measured in Liberty Bay surface
sediments was similar to the range of concentrations (0.009 — 0.15 ug/g)
found by Crecelius and co—workers (1975) in surface sediments from the
relatively remote waters of northern Puget Sound, Hood Canal and the
Strait of Juan de Fuca. The higher mercury concentrations measured
in Liberty Bay were equal to or less than levels (0.069 — 0.52 ug/g)
measured by the above investigators in southern and central Puget
Sound of which Liberty Bay is a part. In no case did the mercury
levels in Liberty Bay sediments approach the high concentrations
(4.0 — 100 ug/g) detected by Crecelius and associates (1975) in sur-
face sediments in Bellingham Bay. These investigators attributed the
source of this mercury contamination to a mercury cell, chior—alkali
plant in Bellingham, Washington that from 1965 to 1971 discharged
substantial amounts of mercury to Bellingham Bay on a daily basis.
Just as the results of the chemical analysis of Liberty Bay waters
failed to show any significant mercury contamination of the water colunni
during the survey, the results of the sediment analyses failed to point
to any major past or present sources of such contamination. The some-
what elevated mercury concentrations measured along the entire length
of sediment cores collected from the upper Bay, particularly behind
the Poulsbo marina breakwater, suggested, however, that relatively
small amounts of mercury had entered the Liberty Bay system over an
extended period of time. This observation was confirmed by the Com-
pliance Monitoring Inspection (EPA, 1975) which found small quantities
of mercury being added to the system via the sewage treatment facilities
in the area as well as from the Torpedo Station plating plant overflow
54
-------
outfall and paint shop storm sewer. Mercury contributed by the STPs
was approximately evenly split between the Poulsbo plant (0.0007 lbs
(0.00032 kg)/day; 46%) and Torpedo Station facility (0.0008 lbs
(0.00036 kg)/day; 52%).
The concentrations of mercury measured in the STP effluents (0.2 —
1.2 ugh) as well as in the Torpedo Station plating plant overflow
(0.3 ugh) and paint shop storm sewer (3.8 ugh) were in general agree—
inent with the levels of mercury reported by Young (1974) in several
municipal wastewater effluents being discharged to southern California
marine waters. The importance of lndustrialdomestic sewage treatment
facilities as contributors of substantial quantities of mercury and
other metals to Puget Sound waters has also been recognized for some
time. Crecelius and his associateS (1975) estimated that prior to
1973, METRO’s West Point sewage treatment plant annually discharged
420 kg of mercury, 250 kg of antimony, and 800 kg of arsenic to the
central Puget Sound basin.
Few, if any, commercially important deposits of mercury ore
(cinnabar) are located near marine waters of the State of Washington
(U.S. Geological Survey, 1966). Although noncommercial mercury ores
appear to be associated with manganese ore deposits on the northwestern
Olympic Peninsula, such ores would not be a direct source of mercury
to the Liberty Bay system.
Nickel concentrations in Liberty Bay surface sediments ranged
from 23 ug/g near the Keyport STP outfall to a high of 112 ug/g behind
the Poulsbo marina breakwater (Fig. 16). With the exception of the
55
-------
Scandi
0 500 1Q00
SCALE IN YARDS
Figure 16. Nickel concentrations in Liberty Bay surface sediments (ug/g dry weight).
REFERENCE STATIONS
HOOD CANAL ( MISERY PT.) 5!
CLAM BAY a
56
-------
relatively high nickel levels measured behind the marina breakwater and
at the Sea Farms hatchery site (110 ug/g), most nickel concentrations
fell within the range of values (25 — 80 ug/g) reported by Huntamer and
Schell (1974) in surface and near—surface sediments from Colvos Passage.
Major potential sources of nickel to Liberty Bay included the Tor-
pedo Station STP (Appendix B) and the Station’s plating plant overflow
bypass (EPA, 1975).
Zinc levels In Liberty Bay surface sediments ranged from 33 ug/g
at Station 9 to 360 ug/g below the Torpedo Station’s mid—storm sewer
(Station S—18). Relatively high zinc concentrations were also measured
behind the Poulsbo marina breakwater (180—250 ug/g) and at the Sea Farms
hatchery site (240 ug/g) (Fig. 17).
The occurrence of high zinc levels below the mid—storm sewer again
points to the used sandblasting sand as a possible significant source
of zinc to the systems Other potentially important sources included
the local STPs (Appendix B) as well as the Torpedo Station plating plant
overflow outfall and paint shop storm sewer (EPA, 1975). Interestingly,
the Poulsbo STP was contributing fifty—six percent of the STP—assocjated
zinc, while the Torpedo Station and Keyport STPs were contributing
twenty—nine and fifteen percent, respectively.
( Sediment Cores ) The results of the metal analyses performed on
the sediment cores are presented in Table 4. Analysis of the core
tops, as well as the middle and bottom sections, yielded results that
were generally characterized by considerable variation between replicate
core samples. This variation made it difficult to determine whether
57
-------
Scandi
0 500 1000
LJI _ 1LJ1 _ 1 1
REFERENCE STAll ONS
HOOD CANAL ( MISERY PT) 54
CLAM BAY 100
SCALE IN YARDS
Figure 17. Zinc concentrations in Liberty Bay surface sediments (ug/g dry weight).
58
-------
Table 4. C ot.-,ri...,.. of Metals ° Cores
—-———
c-ossecLousruas.k
eersy
Coo centrat too
Replicate
Core
Statium dumber
Cote a
Saple
Looatiou
iiglg (dry weight)
Coom
Length
Sediment
Penetration
Aotlirnoy
(Sb)
Aruenic Cadmium
(Am) (Cd)
Chromium
(Cr)
Copper Iron
(Cu) (Fe)
Lead
(Ph)
Maoganeae
Mercury
Miobel
Zinc
1
2
1
2
U’
C-A
(Poulabo Marina)
C— F
(Poulabo Marina)
C— B
(Upper West day)
C— C
(Central Wear say)
C— b
(Lower West day)
C— F
(Lever West Bay)
1
H
B
<0.10
0.70
0.80
14
14
18
4.6
4.0
4.6
73
64
69
54
58
&Q
31,000
31,000
33,000
80
61
54
270
280
300
0.23
0.26
0. 36
69
77
110
130
160
150
27
50
I
H
8
0.70
0.60
0.70
14
12
12
4.0
4.1
4.9
64
64
78
53
60
55
30,000
29,000
33,000
66
60
59
7
290
310
0.30
0.30
0.20
59
50
93
300
250
150
24
48
I
H
8
4.2
1.1
0.80
15
16
13
4.2
4.1
3.3
73
69
52
hi
180
39
41,000
29,000
35,000
83
60
24
300
300
280
0.37
0.35
0.12
55
55
52
150
190
120
25
41
T
H
8
0.90
0.60
0.80
17
15
18
4.3
5.0
4.4
68
67
78
78
62
63
35,000
28,000
39,000
70
63
56
300
4
310
0.37
0.44
0.27
170
63
56
210
150
210
18
43
1
1
H
8
0.20
0.40
0.60
8.0
9.0
7.0
3.0
2.8
3.3
40
41
41
23
23
19
19,000
21,000
20,000
22
22
19
180
180
210
0.10
0.12
79
51
62
76
83
55
14
25
2
T
H
8
0.40
0.50
0.30
9.0
10
8.0
3.3
2.9
2.6
44
42
41
24
24
17
21,000
19,000
15,000
32
29
19
170
170
170
0.13
0.13
0.11
36
75
77
73
86
54
17
33
1
1
H
d
0.40
0.40
0.60
15
14
10
3.5
3.5
3.3
60
51
44
41
39
32
26,000
27,000
24,000
35
35
33
250
250
240
0.15
0.12
0.15
76
82
40
110
160
86
25
30
2
I
H
8
0.10
6.0
0.20
5.0
10
5.0
1.7
1.7
1.3
21
21
26
13
12
a
12,000
13,000
11,000
12
17
14
120
no
3.30
0.082
0.087
0.059
46
31
18
44
51
41
19
25
1
I
H
B
1.0
0.70
0.60
13
10
10
3.1
2.7
3.4
57
46
44
43
34
20
29,000
25,000
23,000
43
36
14
266
210
230
0.17
0.21
0.054
110
100
38
120
110
100
24
50
2
1
H
s
0.60
0.50
0.60
12
9.0
9.0
3.1
3.7
3.7
59
49
48
37
36
28
29,000
25,000
26,000
41
28
15
230
220
240
0.17
0.15
0.20
62
83
40
110
100
77
24
51
1
H
8
0.20
0.30
0.20
5.0
8.0
7.0
1.1
1.1
1.6
18
27
25
10
14
11
10,000
13,000
12,000
8.3
17
20
120
140
140
0.052
0.074
0.10
36
65
20
72
48
41
19
28
1
H
8
0.10
0.10
0.20
7.0
5.0
5.0
1.6
1.1
1.2
35
24
27
24 18,000
12 13,000
6.9 10,000
33
11
8.6
160
120
110
0.14
0,08.3
0.086
90
24
17
110
45
34
17
23
1
2
a I Top of core
H Middle of core
B Bottom of core
-------
or not vertical concentration gradients of selected metals were present
at many of the stations. For the purpose of this report, concentration
gradients were considered to possibly exist at a station only when a
definite gradient trend was observed in both replicate samples.
Although most of the metals failed to exhibit vertical concentration
gradients at most of the stations, weak to strong gradients of all the
metals were observed at one or more of the core sites. The metal levels
measured throughout many of the cores were generally elevated compared
to metal levels in the Hood Canal surface sediment reference sample.
One of the purposes of analyzing sediment cores was to determine
if mercury compounds reportedly applied to oyster beds in 1949 and 1950
to control oyster drills were in high enough concentrations In the sed-
iments to have possibly been the source of the high mercury concentra-
tions reported in Liberty Bay waters. Because the time intervals
covered by the cores could not be determined without additional infor-
mation, It was not known whether or not the cores included sediments
deposited during the period of interest. The relatively short half
life of mercury reported by Crecelius and his associates (1975) in
Bellingham Bay surface sediments, coupled with the knowledge that only
small amounts of mercuric chloride were actually applied to the oyster
beds suggested, however, that the sediments involved were a very
unlikely source of high mercury concentrations In Liberty Bay waters.
This tended to be confirmed by the relatively low mercury levels measured
in all the cores.
The generally higher and more stable concentrations of most of the
metals measured behind the Poulabo marina breakwater (Stations C—A and
60
-------
C—F) are believed to have reflected the relatively rapid accumulation
of sediments in which the metal concentrations had come into equilibrium
with relatively constant sources of metal contamination. If the Torpedo
Station had historically been one of the several point source discharges
contributing significant quantities of metals to the marina sediments,
a decline in surface sediment metal concentrations might have been
expected after treatment of the Torpedo Station plating plant wastes
was begun in February 1975. Nickel concentrations did appear to be
lower in surface sediments than at depth at Station C—A; however, the
reason for this trend was unclear considering the apparent increase in
copper, lead, and mercury levels near the surface of Station C—F.
Continued monitoring of metal concentrations in Liberty Bay sediments
would provide a means of determining the significance of past contri-
butions of metals from the Torpedo Station and other point source
discharges as well as measuring the efficiency of present and future
waste treatment facilities discharging metals to the Liberty Bay system.
Organochlorine Compounds in Surface Sediments
The Liberty Bay surface sediments selected for analysis contained
low to nondetectable levels of BRC (benzene hexachloride), Aroclor
1248/Aroclor 1254 (PCBs) polychlorinated biphenyls, and TCP (total
identifiable chlorinated pesticides) (Table 5). The concentrations
of these compounds measured in the sediment were lower than water—
concentrations of related compounds shown to be acutely toxic to
Pacific oyster embryos (Woelke, 1972; Cummins, Unpublished Data).
Although there was nothing particularly remarkable about the
61
-------
Table 5. Concentrations of Several Organochlorine Compounds in Liberty Bay and Clam Bay Surface
Sediments.
Concentration
ugig (wet weight)
— Station BHCa Aroclor 1248b/Aroclor 1254 b TCPC
Liberty Bay Stations
S—2 0.004 0.004
WSF-3 ND ND ND
(Near Poulsbo STP Outfall)
WSF—5 0.004 0.021 0.025
(Oyster Hatchery Site)
C’
WSF—13 ND 0.004 0.004
(Keyport STP Outfall)
SF—16 ND 0.006 0.006
WS-17 ND ND ND
(NTSe Paint Shop Storm
Sewer Outfall)
Reference Stations
Clam Bay ND 0.013 0.013
a BHC — “Benzene hexachioride”
b Polychiorinated biphenyls (PCB’s)
c TCP (Total identifiable chlorinated pesticides)
d ND (Not detected)
e N1 S Navy Torpedo Station
-------
levels of organochiorine compounds observed, it is of interest to
note that surface sediments collected from Station WSF—5 near the
Sea Farms hatchery site contained more BHC, Aroclor 1248/Aroclor 1254,
and TCPs than any of the other sediments analyzed.
Sulfides in Surface Sediments
Concentrations of total sulfides in Liberty Bay surface sediments
ranged from 25 ug/g at Station S—9 to a high of 1300 ug/g at the Sea
Farms hatchery site, Station WSF—5 (Fig. 18). This range of sulfide
levels was within the range of concentrations (<10 — 3770 ug/g)
reported by O ’Neal and Sceva (1971) in sediments from estuarine and
marine harbors in the Pacific Northwest.
Shellfish —
Metal Concentrations
Metal concentrations measured in the shellfish collected from
Liberty Bay, Clam Bay, and Hood Canal are presented in Table 6.
( Interspecific Differences ) With some exceptions, there was a
general similarity between the metal concentrations in shellfish
collected from Liberty Bay as well as between these shellfish and
the Clam Bay and Hood Canal stocks. Although some of the variation
in metal concentrations could be attributed to differences In station
location, as will be discussed later, the most prominent source of
variation appeared to be related to interspecific differences in the
metal content of the various species of shellfish analyzed. Metal
levels characterizing Japanese and native littleneck clams were quite
63
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SCALE IN YARDS
Figure 18. Total sulfide concentrations in Liberty Bay surface sediments (ug/g dry
weight).
REFERENCE STATIONS
HOOD CANAL MLSERY P1 4H
CLAM BAY 1/
0 500 1000
64
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16112 6. Conceotratinna of Metals in Shellfish Collected from Liberty Bay. Clam Say, and Bond Canal .
Station
Liberty Bay Statinna
Date
Concentration
pg/p (wet weight)
Antimony Araenic Cadmii Chrnmia Cnpper Lead Mercury Nickel SeLenium Zinc
(Sb) (Pa) (Cd) (Cr) (Cu) (Pb) (Np) (Ni) (Be) (Zn)
Sf—i
(Upper West Bay)
9—12—li Pacific Oysters
Crussoetro< ‘/gCe
<0.020 0.20 1.1 0.50 7.6 1.4 0.006 2.5
0.040 150
Sf— S
(Oyster Ratchery Site)
9—12—75 Japanese Littleneck
Clara
Venerupie japonica
<0.020 1.0 0.44 0.90 1.9 2.7 0.024 2.7
0.23 19
Japanese LLttlenark <0.030
Class
NatLve Littleneck Ciame <0.020
Vensrupie aiaininea
Japanese Littlaneck <0.020
Clams
Native littleneck Clams <0.030
Japanese tittisneek 0.030
Class
Bative Littleneck Clams 0.020
Japanese Littlaneek Class 0.050
Native tittlsneck Clams <0.030
Japanese Littleneck <0.030
Class
Native Littleneck Clams <0.030
Native Littleneck Clams 0.020
Butter Clssa <0.030
Saxidosua giganieua
Beferonse Ststinns
Hood Canal (Miaery Pnlnt)
9—14—75 Japanese Littleneck
Clams
0.040 0.50 0.35 0.70 2.6 1.2 0.013 1.8
0.020 15
0 ’
I-n
Sf—6
(West Central Nay)
Of—lO
(Sosthweet Say) —
Sf— 12
(Southeast Bay)
Sf—l a
(Koyport S IP Ontfa li)
Sf—i4
(Hasika Say)
Sf—15
(Barrage Pniet)
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
9—12—75
0.70
0.45
0.60
1.8
1.7
0.023
1.7
0.10
17
1.5
0.50
0.50
1.8
2.0
0.015
1.5
0.19
19
1.0
0.53
1.6
1.6
1.1
0.024
2.1
0.25
18
1.2
0.57
0.70
0.92
1.1
0.019
1.1
0.040
16
1.1
0.35
0.70
1.6
1.2
0.020
1.7
0.070
19
1.5
0.59
0.70
0.68
1.9
0.012
1.4
0.050
18
0.80
0.38
0.60
1.9
0.96
5.016
1,4
0.050
20
1.1
0,45
0.70
1.0
1.1
0.016
2.3
<0.020
25
0.60
0.43
1.8
1.9
1.1
0.013
2.7
0.16
21
1.2
0.47
1.4
1.7
1.2
0.010
15
0.040
17
1.2
0.49
1.0
2.1
1.0
0.012
2.0
0.040
1)
2.2
0.24
1.9
3.8
1.2
0.017
7.8
0.040
18
Clan Bay
9—14—75 Native Littleneck Clams <0.030
1.2 0.36 0.90 1.8 1.2 0.013 3.6 0.000 15
-------
similar. Pacific oysters collected from upper Liberty Bay (Station
Sf—i), however, contained the highest concentrations of cadmium (1.1
ug/g), copper (7.6 ug/g), and zinc (150 ug/g), while exhibiting the
lowest levels of arsenic (0.20 ug/g) and mercury (0.008 ug/g). Marked
interspecific differences in trace metal uptake was demonstrated a
number of years ago in several species of shellfish taken from New
Zealand waters (Brooks and Rumsby, 1965). Interestingly, oysters ana—
lyzed during these studies in New Zealand, Ostrea sinuata , as well as
American oysters, C. virginica , collected from Mobile Bay and the
Atlantic coast also exhibited high copper and zinc levels relative to
the concentrations of other metals present (Shuster and Pringle, 1969;
Kopfler and Mayer, 1973). It should be noted, however, that the oysters
sampled during the Liberty Bay survey were collected from Coast Oyster
Company beds that had been planted some time earlier with oysters grown
in other waters. The metal content of these shellfish prior to their
transfer to Liberty Bay could have Influenced their metal content at
the time of our sampling.
Butter clams collected just outside Liberty Bay (Station Sf—15)
contained the highest arsenic concentrations (2.2 uglg) and the second
highest levels of copper (3.8 ugfg) and nickel (7.8 ug/g). The highest
nickel concentration (15 ug/g) was exhibited by the native littleneck
clams collected at Station Sf—14 on Nesika Bay. Japanese littleneck
clams collected at the same station exhibited nickel levels of o.nly
2.7 ug/g. The 15 ug/g value appeared to be a possible anomaly because
of the uncharacteristic gap between the nickel concentrations of these
66
-------
two species of clams. This high value should not be disregarded, how-
ever, without additional confirmation.
( Distribution ) The distribution of the various shellfish—associated
metal levels throughout the Liberty Bay system is shown in Figures 19—28.
Comments about the distribution of these metals within the survey area
are based solely on their concentrations in Japanese and native little-
neck clams. These species were selected for this “indicator” role
because of the broad geographic coverage they provided as well as the
apparent similarity in their metal uptake patterns.
Although no pronounced station—associated differences were apparent,
clams from Liberty Bay proper tended to exhibit higher concentrations
of arsenic, cadmium, lead, mercury, and selenium, while chromium and
copper levels tended to be higher in clams collected from stations just
outside the Bay. Except for the 15 ug/g nickel concentration measured
at Station Sf—14 in Nesika Bay, nickel, antimony and zinc levels remained
about the same throughout the Liberty Bay system.
Several of the metals levels measured in Japanese and native little-
neck clams appeared to be correlated, to varying degrees, with companion
surface sediment metal concentrations. The strongest positive correla-
tion observed In both species involved increasing shellfish and surface
sediment lead levels toward the head of the Bay. Comparison of metal
levels characterizing shellfish and sediments from Nesika Bay and
waters adjacent to the Torpedo Station was not possible because compan-
ion samples were not collected in these areas.
( Comparative Data ) Metal levels measured In shellfish from Liberty
67
-------
8BUTTER CLAMS
J JAPANESE LiTTLENECK CLAMS
N NATIVE LiTTLENECK CLAMS
P PACIFIC OYSTERS
<- LESS THAN
0 500 1000
SCALE IN YARDS
Figure 19.
Antimony concentrations in several species of Liberty Bay shellfish (ug/g
vet weight).
REFERENCE STATIONS
HOOD CANAL ( M SERY PT.) J 0.040
CLAM BAY N
-------
B 8UTTER CLAMS
J JAPANESE LITTLENECK CLAMS
N NATIVE LITTLENECK CLAMS
P PACIFIC OYSTERS
0 500 1000
SCALE IN YARDS
Figure 20. Arsenic concentrations in several species of Liberty Bay shellfish (ug/g
wet weight)
REFERENCE STATIONS
HOOD CANAL I MISERY PT I J 050
CLAM BAY N ii
B
N 12 •
69
-------
B-BUTTER CLAMS
J-JAPANESE LITTLENECK CLAMS
N NATIVE UTTLENECK CLAMS
P-PACIFIC OYSTERS
Q 500 1000
SCALE IN YARDS
Figure 21, Cadmium concentrations in several species of Liberty &iy shellfish (ug/g
wet weight).
REFERENCE STATIONS
HOOD CANAL ( MISERY PT. J O 35
CLAM BAY N 0 36
N
B
70
-------
J JAPANESE LITTLENECK CLAMS
N NATIVE LITTLENECK CLAMS
P PACIFIC OYSTERS
l igure 22, Chromium concentrations in several species of Liberty Bay shellfish (ug/g
wet weight).
REFERENCE STATIONS
HOCD CANAL ) MISERY PT) J 070
CLAM BAY N 0 90
J 0 80
N O 5O
I
B BUTTER CLAMS
I
0 500 1000
B
N
S
SCALE IN YARDS
71
-------
Scandi
B-BUTTER CLAMS
J -JAPANESE LITTLENECK CLAMS
N-NATIVE UTTLENECK CLAMS
P-PACIFIC OYSTERS
0 500 1000
SCALE IN YARDS
Figure 23.
Copper concentrations in several species of Liberty Bay shellfish (uglg wet
weight).
REFERENCE STATIONS
HOOD CANAL ( MISERY PT.) J 2 8
CLAM BAY N 1.8
B 3.8
N 2.1 .
72
-------
B 8UTTER CLAMS
J JAPANESE LITTLENECK CLAMS
N NATIVE LITTLENECK CLAMS
P PACIFIC OYSTERS
0 500 1000
LiLJ — —
SCALE IN YARDS
Figure 24.
Lead concentrations in several species of Liberty Bay shellfish (ug/g wet
weight).
REFERENCE STATIONS
HOOD CANAL ) MISERY PT) J 12
CLAM BAY N L2
B
N
S
73
-------
S can di
B BUTTER CLAMS
J JAPANESE LITTLENECK CLAMS
N NATIVE LITTLENECK CLAMS
P PACIFIC OYSTERS
Figure 25. Mercury concentratiors in several species of Liberty My shellfish (ug/g
wet weight).
REFERENCE STATIONS
HOOD CANAL I MISERY PT,) J 0.013
CLAM BAY N 0.013
.1 0.024,
J 0.023
0.015
B
N 0.012
SCALE IN YARDS
74
-------
Scand
B 8UTTER CLAMS
J JAPANESE LITTLENECK CLAMS
N NATIVE LITTLENECK CLAMS
P PACIFIC OYSTERS
500 p000
jw r r
SCALE IN YARDS
Ii ’
REFERENCE STATIONS
HOOD CANAL ( MISERY PT ) j t8
CLAM BAY N 3 6
B
N
Figure 26.
Nickel concentrations in several specie8 of Liberty Bay shellfish (ug/g
wet weight).
75
-------
B-BUTTER CLAMS
J -JAPANESE LITTLENECK CLAMS
N NATIVE LITTLENECK CLAMS
P-PACIFIC OYSTERS
LESS THAN
SCALE N YARDS
Figure 27. Selenium concentrations in several specie8 of Liberty Bay shellfish (ugfg
wet weight).
REFERENCE STATIONS
HOOD CANAL ( MISERY PT ,) 3 0.020
CLAM BAY N 0.080
B
N
76
-------
8 BUTTER CLAMS
JJAPANESE LITTLENECK CLAMS
N NATIVE LITTLENECK CLAMS
P PACIFIC OYSTERS
0 500 1000
-I _ J-l _ J- -
SCALE IN YARDS
Figure 28, Zinc concentrations in several species of Liberty Bay shellfish (ugig wet
weight).
REFERENCE STATIONS
HOOD CANAL ( MISERY PT.) J 15
CLAM BAY N 15
N
B 18.
77
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Bay, Clam Bay, and Hood Canal by the various state and federal agencies
that responded to the Sea Farms report of high mercury concentrations
in Liberty Bay waters are presented in Tables 7 to 10. Included in
these tables are the data provided by FDA showing the range of metal
levels in shellfish collected in 1970 and 1971 from various “open”
and “closed” shellfish growing areas along the west coast. The “open”
or “closed” classification of these areas was based on State evaluations
of the actual or potential bacteriological quality of the water (Personal
Communication, James Davis, U.S. FDA, Seattle, WA).
In addition to the reasonable agreement between the results of the
various laboratories, one of the most distinctive features of these data
was the relationship between metals in shellfish from the Liberty Bay
system compared to levels in shellfish from the other areas. The average
concentrations of arsenic, cadmium, lead, and nickel measured by EPA
in all species collected from the Liberty Bay system exceeded the average
concentrations of these metals in the same species from other west coast
waters as well as from Clam Bay and Hood Canal. Average Liberty Bay
copper concentrations were less than the average levels of copper in
shellfish from the other areas, while average Liberty Bay mercury con-
centrations were greater than the Clam Bay and Hood Canal values, but
less than the west coast average. The relation of Liberty Bay zinc and
copper levels to the levels measured in shellfish from the other areas
was not as well defined. In most cases, however, the average concentra-
tions of the metals in Liberty Bay shellfish were greater than or equal
to the average levels measured in shellfish collected elsewhere.
78
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TABLE 7. Concentrations of Metals in Japanese Littleneck Clams, Venerupis daponica from Liberty Bay, Hood
Canal. and Other West Coast Locations .
West Coast Liberty Bay Liberty Bay Liberty Hay Hood Canal EPA
FDA Mean EPA Mean FDA Mean DSHS 5 Reference StStiOflc
. . Nlement (Range)b (Range)C (Range) ’
Concentration jig/g (wet weight )
Antimony (Sb) <0.030 0.040
(<0.020—0.050)
Arsenic (As) 0.10 0.87 0.50
(0.0—0.42) (0.60—1.1)
Cadmium (Cd) 0.30 0.43 0.15 0.36 0.35
(0.020—0.53) (0.35—0.53) (0.13—0.16)
Chromjur (Cr) 1.1 1.1 0.45 0.25 0.70
(0.0—3.2) (0.60—1.8) (0.38—0.52)
Copper (Cu) 2.3 1.8 2.5 2.0 2.8
(0.78—7.6) (1.6—1.9) (2.5—2.6)
Lead (Pb) 0.45 1.5 ND 0.20 1.2
(0.0—1.2) (0.96—2.7)
Mercury (Hg) 0.16 0.020 0.025 0.02 0.013
(0.050—0. 78) (0.013—0.024) (0.02—0.03)
Nickel (Ni) 2.0 2.1 2.3 1.8
(1.0—2.9) (1.4—2.7)
Selenium (Se) 0.14 0.020
(0.050—0.25)
Zinc (Zn) 14 19 13 14 15
(8.7—20) (3.7—21) (10—15)
a Values reduced to two significant figures where appropriate.
b u.s. Food and Drug Administration, “Table of Analytical Values for Heavy Metals in Shellfish Taken From
Various West Coast Estuaries in 1970—71.”
c U.S• Environmental Protection Agency. Collected 9/12—14/75.
d U.S. Food and Drug Administration. Collected 9/22175, Nesika Bay.
e Washington State Department of Social and Health Services. Collected 9/22/75, Nesika Hay.
ND Not detected.
79
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Table S. Concentrations of Metals in Native Littleneck Clans, Venerupis sta ninea, from Liberty Bay, Clam Bay,
and Other West Coast Locations.a
West Coast Liberty Bay Liberty Bay Clan Bay EPA
FDA Mean EPA Mean DS1ISd Reference Station 0
Element (Range)b (Range) °
Concentration pg/g (wet weight )
Antimony (Sb) ——— <0.025 ——— <0.030
(<0.020—0.030)
Arsenic (As) 0.08 1.3 ——— 1.2
(0—0.25) (1.1—1.5)
Cadmium (Cd) 0.29 0.51 0.36 0.36
(0.09—0.54) (0.45—0.58
Chromium (Cr) 1.1 0.83 0.28 0,90
(0—2.3) (0.50—1.4)
Copper (Cu) 2.0 1.4 1.4 1.8
(0.9—4.6) (0.68—2.1)
Lead (Pb) 0.22 1.4 0.24 1.2
(0—1.1) (1.0—2.0)
Mercury (Hg) 0.05 0.014 0.04 0.013
(0—0.12) (0.010—0.019)
Nickel (Ni) 1.2 3.9 1.92 3.6
(0.38—1.9) (1.1—15)
Selenium (Se) —— <0.63 — 0.080
(<0.020—0.19)
Zinc (Zn) 26 18 12 15
(12—160) (13—25)
a Values reduced to two significant figures where appropriate.
b U.S. Food and Drug Administration, “Table of Analytical Values for Heavy Metals in Shellfish Taken From
Various West Coast Estuaries in 1970— il.”
c U.S. Environmental Protection Agency. CoLlected 9/12—16/75.
d Washington State Department of Social and Health Services. Collected 9/23/75, southwest Bay.
80
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TABLE 9. Concentrations of Metals in Butter Clams, Sarcidomu8 g-i ganteus, from Liberty Bay and Other West Coast
Locations .
West Coast Liberty Bay
FDA Mean EPAC
Element (Range)b
Concentration igfg (wet weight )
Antimony (Sb) ——— <0.03
Arsenic (As) 0.36 2.2
(0—0.87)
Cadmium (Cd) 0.05 0.24
(0—0.14)
Chromium (Cr) 1.6 1.9
(0.33—3.7)
Copper (Cu) 6.3 3.8
(3. 7—8.2)
Lead (Pb) 0.29 1.2
(0—1.3)
Mercury (Hg) 0.30 0.017
(0.086—0.60)
Nickel (Ni) 1.5 7.8
(0.2 3—2.7)
Selenium (Se) 0.04
Zinc (Zn) 15 18
(10—16)
a Values reduced to two significant figures where appropriate.
b U.S. Food and Drug Administration, “Table of Analytical Values for Heavy Metals in Shellfish Taken From Various
West Coast Estuaries in 1970—71.”
C U.S. Environmental Protection Agency. Collected 9/12/75.
81
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Table io. Concentrations of Metals in Pacific Oyeters C aesoatrea gigcza, from Liberty Bay and Other West Coast
ti 0 a .
West Coast Liberty Bay Liberty Bay Liberty Bay Liberty Bay
FDA Mean EPAC FDA Mean DSHS Mean NMFS Meai
Element (Ran e)b (Rau e)d (Range)e (Range)
Concentration g/g (vet weig )
Antimony (Sb) <0.020
Araenic (As) 0.06 0.20
(0—0.23)
Cadmium (Cd) 0.94 1.1 1.0 1.3
(0.53—1.7) ——— (1.2—1.5)
Chromium (Cr) 0.32 0.50 0.25 0.27
(0—1.3) (0.23—0.27) (0.25—0.28)
Copper (Cu) 20 7.6 1.1 15
(6.4—50) (0.97—1.3) (12—17)
Lead (Pb) 0.32 1.4 <0.18 0.22
(0—2.0) (ND—0.18)
Mercury (Hg) 0.05 0.008 0.015 0.02 0.03
(0—0.12) (0.010—0.020) 1.01—0.04) (0.02—0.04)
Nickel (Ni) 0.78 2.3 1.8
(0—1.8) (1.5—2.0)
Selenium (Se) 0.040
Zinc (Zn) 150 150 160 200
(66—300) (140—170) (170—230)
a Values reduced to two significant figures where appropriate.
b U.S. Food and Drug Administration, “Table of Analytical Values for Neavy Metals in Shellfish Taken from VarioUS
West Coast Estuaries in l970 7l.”
c u.s. Environmental Protection Agency. Collected 9/12/75.
d U.S. Food and Drug Administration. Collected 9/23/75, central and upper Bay.
e Washington State Department of Social and Health Services. Collected 9/23/75, central and upper Bay.
f National Marine Fisheries Service. Pacific Utilization Research Center. Collected 8/15/75, See Farms site.
ND Not detected.
82
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The slightly elevated nature of many of the metal concentrations
characterizing Liberty Bay shellfish tended to confirm the historical
fact that metallic wastes have been discharged to the system for many
years. However, the general similarity between the metal levels in
shellfish from Liberty Bay, Hood Canal, Manchester, and other west
coast areas suggested that, from the standpoint of trace metal uptake,
metallic discharges to the Liberty Bay system had not seriously Impacted
the shellfish populations sampled. Significantly, the levels of mercury
measured in shellfish from Liberty Bay (0.008 — 0.024 ug/g) as well as
from the Clam Bay and Hood Canal reference stations (0.013 ug/g) were
well below the proposed Food and Drug Administration (FDA) action level
of 0.5 ug/g (wet weight) for mercury in fish and shellfish (U.S. FDA,
1974). These shellfish would, therefore, have been considered safe
for human consumption from the standpoint of their mercury content.
Their relatively low mercury content also suggested that it was unlikely
that large continuous or intermittent discharges of mercury had been
made to the Liberty Bay system over an extended period. This becomes
particularly evident when considering the ability of fish and shellfish
to exhibit mercury levels that are hundreds or thousands of times
greater than the mercury concentrations of the waters in which they are
living (Peakall and Lovett, 1972).
Organochiorine Concentrations
The levels of polychlorinated biphenyls (PCBs) measured in shellfish
from Liberty Bay are presented in Table 11.
83
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Table ii. Concentrations of Polychiorinated Biphenyls in Shellfish
Collected from Liberty Bay.
Concentration
ng/g (wet weight)
Aroclor Aroclor
1242 1248/1254
<10 <20
Total PCB concentrations (Aroclor 1242 plus Arocior 1248 and 1254) meas-
ured in Liberty Bay shellfish ranged from <20 ng/g at Stations Sf—i and
Sf—5 to 92 ng/g at Station Sf—10.
The total PCB concentration measured In Japanese Littleneck Clams
from Station Sf—10 (92 ng/g) was higher than the levels of PCBs (Aroclor
1254 and Aroclor 1260) measured by Claeys and coworkers (1975) in cackles,
Cllnocardium nuttalili , and Eastern softsheil clams, arenaria , from
several Oregon estuaries. Although this determinate level was believed
to reflect limited inputs of PCBs to the Liberty Bay system, it was
considerably lower than the PCB concentrations (390 — 1170 ng/g) meas-
ured in Asiatic clams, Corbicula fluminea , from the Columbia River
estuary (Claeys etal., 1975).
Total
<20
Station
Species
Sf —i
(Upper West Bay)
Sf—5
(Oyster Hatchery
Sitc)
Pacific Oysters
Crassostrea gigas
<10
<20
<20
Japanese Littleneck
Clams
Venerupis japonica
Sf—lU
(Southwest Bay)
Japanese Littleneck
Clams
46
46
92
84
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Fish Muscle Tissue —
Metal Concentrations
Presented in Table 12 are the concentrations of metals measured
in the muscle tissues of various bottom fishes collected during the
survey. Unlike the oysters and clams, the fishes sampled from the
Liberty Bay system were free to move throughout the system as well as
into neighboring Puget Sound waters. The metal concentrations in their
tissues were considered, therefore, to primarily reflect conditions
throughout this range rather than at any one station.
Few differences were observed in the concentrations of the various
metals measured in the fishes from Liberty Bay, regardless of species
or collection site. The metal concentrations in the muscle tissues of
these fishes were also similar to levels measured in the fishes from
the Hood Canal and Clam Bay reference stations and generally corre-
sponded to levels measured in fishes from central Puget Sound (Huntamer
and Schell, 1974). The only major difference involved the 14 ug/g
arsenic concentration measured in the Clam Bay rock sole compared to
the relatively low range of arsenic levels (0.10 — 0.70 ug/g) found in
the other fishes collected. This dissimilarity was not attributable to
interspecific differences or variations in size since the sample popu-
lation exhibiting the low arsenic levels contained rock sole of compa-
rable size. The relatively high arsenic value did correspond, however,
to the range of levels (5.4 — 13.8 ug/g) reported by Huntamer and Schell
(1974) in the muscle tissues of flat fishes from Colvos Passage and
Commencement Bay. Although the high arsenic level (14 ug/g) may have
85
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Station Date Species
Table 12. -i” - of in the of Bottom Fishes ‘‘te 4 from tiber ” Bay, Clam “fl ’ hood Canal.
Concentration
g/ (wet weight)
Length Antimony Arsenic Cadmium Chromium Copper Iron Lead Manganese Mercury Nickel Selenium Zinc
( em) (Sb (As) (Cd) (Cr) (Cu) (Fe) (Pb ) (Mn) ( Hg) (Ni ) (Se) (Zn)
Liberty Bay Stations
WSF—3 9—15—75 Great Scuipin 28 <0.020 <0.10 0.10 0.50 0.40 6.0 <1.0 0.20 0.047 2.0 0.040 8.2
(Near Poulabo SF? Outfall) !4o wcephaiu s
piaaanthocepRolua
NSF—S 9—17—75 Buffalo Soulpin 25 <0.020 <0.10 0.10 0.40 0.47 10 <1.0 0.30 0.047 7.9 <0.030 17
(Oyster Hatchery Site) Knophrya biaon
WSF—13 9—15—75 C — 0 Sole 30 <0.020 0.20 0.10 0.30 0.29 3.9 <1.0 <0.20 0.15 1.5 <0.020 6.0
(Keyport 5FF Outfall) Pl zoxninhth9s
006 flOBU S
SP— 16 9—17—75 Rock Sole 30 0.020 0.70 0.10 0.40 0.29 4.8 <1.0 0.60 0.066 1.0 0.080 6.9
(NTSa SF? Outfall) Lepi dopsetta
bilineata
9—17—75 Rock Sole 20 0.050 0.10 0.10 0.40 0.39 4.8 <1.0 0.40 0.036 1.9 0.050 7.7
Lepidopoetta
bilineata
WSF—19 9—17—75 Rock Sole 30 0.020 0.70 0.10 0.40 0.56 4.2 <1.0 0.20 0.054 7.9 0.090 7.6
(Near Plating Plant Overflow L. bilineata
Outfall)
9—17—75 Great Sculpin 30 0.040 <0.10 0.10 0.40 0.46 7.4 <1.0 0.40 0.074 <0.50 0.080 8.5
M. po Z acw2thocephaiue
Staghorn Sculpin
Leptooottus arnutue
Rock Sole
1. bilineata
Reference Station 9
Rood Canal (Misery Point)
Clam Bay
9—16—75
9—28—75
a1 S Navy Torpedo Station
18 0.030 0.20
28 0.050 14
0.10 0.50 0.48 8.7 <1.0 0.30 0.021 1.9 ——
<0.10 0.50 0.77 8.7 1.0 0.20 0.030 1.4 0.18
9.0
6.8
-------
been related to the relative proximity of the Clam Bay station to the
Tacoma smelter (ASARCO) or other local sources of arsenic, the concen-
trations of arsenic measured in fishes from the Liberty Bay and Clani
Bay stations appeared to be disproportionately low and, therefore,
should be viewed with caution until they are confirmed.
Just as in the case of the shellfish, the levels of mercury
meas ured in the muscle tissues of the fishes collected from Liberty
Bay and the survey reference stations (0.030 — 0.15 ug/g) were below
the proposed FDA action level for mercury in fish and shellfish of
0.5 ugfg (wet weight) (U.S. FDA, 1974).
Biological Characterization
Phytoplankton Production —
As mentioned earlier in the report, dense phytoplankton popula-
tions, of “bloom” proportions, were observed in Liberty Bay during
the survey September 15, 1976. Based on total organic carbon (TOC)
measurements (Table 2) and the tea—colored character of the popula-
tions, the bloom appeared to be located in the surface waters near
Station WS—7 (Nid—Bay) during low tide. Under high tide conditions,
the bloom was observed In surface waters near the Poulsbo STP outfall
(Station WSF—3) and at the Sea Farms hatchery site (Station WSF—5).
The major phytoplankton and protozoan species present in the
bloom as well as in other selected Liberty Bay surface waters during
and following the survey are presented below.
87
-------
Date Station Preservative Species
9—15—76 WSF—5 Formalin (Dinoflagellates)
(Phytoplankton bloom Prorocentruni gracile
observed) Gymnodiriium splendens
Glenodinium sp.
Ceratlum fusus
Gyrodinium spirale
(Diatoms)
Coscinodiscus wailsii
(Ciliate Protozoans)
Parundella lagena
9—15—76 W—l1 Fornialin (Dinoflagellates)
(No phytoplankton Prorocentruni gracile
bloom observed)
(Diatoms)
Thalassiosira sp.
(Ciliate Protozoans)
Parundella lagena
10—7—76 WS -7 Lugol’s (Dinoflagellates)
Solution
Prorocentrum gracile
(No phytoplankton Gymnodinium variable (minini9)
bloom observed) Ceratium fusus
Glenodiniuin sp.
Gyrosigma fasciola
Peridiniuni minutum
(Diatoms)
Nitzschia closterium
Nitzschia seriata
Skeletonema costatum
Coscinodiscus wailsii
Thalassiosira sp.
88
-------
Date Station Preservative Species
(Blue—Green Algae)
Spirulina sp. ?
(Ciliated Protozoans)
Parundella lagena
Stenosomella pacifica
10—7—75 North of Lugol’s (Dinoflagellates)
Poulsbo Marina Solution
Prorocentrum gracile
Gymnodinium variable (minima)
Glenodinium sp.
Gyrosigma fasciola
Perldiniuin ovatum
(Diatoms)
Nitzschia closterium
Nitzschia seriata
Nitzschia sp.
Skeletonema costatum
Coscinodiscus wailsii
Thalassiosira rotula
Chaetoceros vanheurkil
(Blue—Green Algae)
Spirulina sp. ?
(Ciliate Protozoans)
Stenosomella pacifica
The algal bloom was composed primarily of the dinoflagellates
Prorocentrum gracile and Gymnodinium splendens . The concentrations
of these organisms present in surface waters at Station WS—7 during
low tide (September 15, 1975) were 2.7 X io 6 and 3.7 X l0 cells/mi,
respectively. Several of the species identified in Liberty Bay waters
following the survey (October 7, 1975) may also have been present
89
-------
during the bloom September 15, 1975. Formalin preservation of the
survey samples may, however, have resulted in the destruction or
deformation of the more fragile forms.
The organism tentatively identified as the blue—green alga,
Spirulina sp., was thought to possibly be a bacterium. This organism,
together with P. gracile and G. spendens , were the predominate species
present at Station WS—7 and north of the Poulsbo marina on October 7,
1975. There was also some doubt about the identity of the dinoflagel—
late, Gymnodinium variable (minima). It was recognized that these
organisms may have represented more than one species or perhaps the
spores of symbiotic Gymnodiniods (Personal Communication, Dr. Richard
Steele, EPA, Narragansett, RI).
When discussing algal blooms, questions are usually raised as to
the cause of the blooms. Based on the work of Lincoln and Collias
(1975), substantial blooms of phytoplankton can be supported in Liberty
Bay as a result of nutrients entering the Bay from Port Orchard. As
stated earlier, these investigators believed that nitrate and silicate
were the nutrients limiting algal growth in the Port Orchard system.
Lincoln and Collias (1975) also identified biological decomposition
and slow flushing as the processes responsible for the relatively high
ammonia levels measured in the deeper portions of the Bay. The origin
of the decomposing organic material and the possible stimulatory effect
of the elevated ammonia levels on algal growth were not made clear.
They Implied that the decomposition of the algal biomass produced
during the spring phytoplankton bloom was primarily responsible for
90
-------
the generally higher ammonia concentrations. Considering the apparent
nitrate limited character of Liberty Bay waters, ammonia and organic
matter being discharged to the Bay by local STPs (Poulsbo’s primary
treatment plant in particular) should also be considered as potentially
important nitrogen sources capable of supporting localized algal blooms.
Oyster Embryo Response —
Water
The response of Pacific oyster embryos to seawater collected from
the Liberty Bay system, Clam Bay, and Hood Canal is presented in Tables
13 and 14. These data are plotted in Figures 29—32 to show the vertical
and horizontal differences in embryo response measured September 15,
1975 under conditions of low and high tide. Although oyster embryo
development and survival are the response parameters discussed below,
shell growth was also observed to be a sensitive measure of water qual-
ity. In fact, pronounced differences in the size of normally developed
larvae revealed subtle adverse effects not reflected by larval develop-
ment or survival.
( Survival) Low Tide — Relative good larval survival (89.7 — 1O42 )
was observed in waters collected from all depths at the Sea Farms site
(Station WSF—5) and lower Bay (Stations W—ll and WSF—13) during low -
tide. Survival in these waters was similar to that observed in the
Clam Bay and Hood Canal samples (92.9 — 105%). Larval survival in sur-
face waters from Station WSF—3 near the Poulsbo STP outfall was only
71.5%. However, no larvae survived exposure to the surface waters from
Station WS—7 in central Liberty Bay to which the algal bloom seemed to
91
-------
a Relative to survival in Clam Bay (bioassay control) seawater.
b Carry along control: 94.5% survival.
Table 13. Pacific Oyster
Embryo Survival (48-Hour)
in Liberty Bay, Clam Bay, and Hood Canal Waters.
Tidal
Stage
Sampling Depth
Surface
Liberty Bay
Mean Per
Cent Relative
Survivala
Stationsb
Stations
Reference
WSF-3
71.5
WSF-5 WS-7
104 0
W-ll
85.2
WSF- 13
100
Hood Canal
105
Clam Bay
105
Low
Mid-Depth
8 8.3
89.8 61.6
98.4
101
92.9
101
Bottom
90.7
94.8 94.5
96.7
89.7
101
94.1
(Station Mean)
(83.5)
(96.2) (52.0)
(93.4)
(96.9)
(99.6)
(loG)
High
Surface
41.6
20.2
77.5
79.6
96.3
105
105
Mid-Depth
99.9
97.9
92.4
83.5
83.7
92.9
101
Bottom
100
89.8
81.1
91.5
99.4
101
94.1
(Station Mean)
(80.5)
(69.3)
(83.7)
(84.9)
(93.1)
(99.6)
(100)
-------
Table 14. Pacific Oyster Embryo Development (48—Hour) in Liberty Bay, Clam Bay, and Hood Canal Waters.
a Clam Bay (bioassay control): 0.4% abnormality
b Carry along control: 0.5% abnormality
Tidal Stage
Sampling Depth
Liberty
Mean Percent Abnormal Larvae
Reference Stations
Bay Stations
WSF—3
WSF-5
WS-7 W-ll
WSF-l3
Hood Canal
Clam Bay
Surface
3.1
1.7
- 0.4
0.5
0.8
0.7
Low
Mid-Depth
0.4
1.3
1.1 1.1
0.7
1.1
0.5
Bottom
0.8
0.4
0.4 1.4
0.6
1.2
0.4
(Station Mean)
(1.4)
(1,1)
- (0.97)
(0.60)
(i.o)
(o. )
High
Surface
6.4
95.8
0.7
25.3
4.4
0.8
0.7
Mid—Depth
0.8
0.7
1.1
0.8
2.9
1.1
0.5
Bottom
0.3
0.0
0.2
1.3
0.7
1.2
0.4
(Station Mean)
(2.5)
(32.2)
(0.67)
(9.1)
(2.7)
(i.o)
(0.5)
-------
SAMPLE SITE
SURFACE
MI D DEPTH
BOTTOM
0 500 1000
SCALE IN YARDS
Figure 29, Relative per cent survival of Pacific oyster embryos in Liberty Bay waters
collected during low tide.
REFERENCE STATIONS
HOOD CANAL ( MISERY PT,) 105
92.9
101
CLAM BAY 105
101
94.1
94
-------
be primarily confined. A well defined vertical response gradient was
also observed at this station, with 61.6% and 94.5% survival occurring
in middepth and bottom waters, respectively.
High Tide — Under high tide conditions, a slight general decline
in survival was observed in waters from Stations W—1l and WSF—13, with
survival values ranging from 79.6% to 96.3%. Although larval survival
in surface waters from Station WSF—3 dropped from 71.5% to 41.6%, the
most pronounced changes in survival associated with increased tide
height were observed in waters from Stations WSF—5 and WS—7. The per-
centage of larvae surviving in surface waters from Station WS—7 jumped
from 0% to 77.5%, while larval survival in surface waters from Station
WSF—5 declined from 104% to 20.2%, reflecting a substantial reduction
in water quality in the vicinity of the Sea Farms seawater intake.
These changes In larval response appeared to be directly related
to the tidal movement of the algal bloom away from Station WS—7 toward
the Sea Farms hatchery site (Station WSF—5), This shift In the location
of the bloom was observed visually as well as being reflected by pro-
nounced increases in surface water total organic carbon (TOC) levels
at Stations WSF—3 and WSF—5 (Table 15). The possible adverse influence
of algal bloom conditions on larval survival was also supported by
correlation analysis showing a high negative correlation between TOC
levels and larval survival during both high and low tide (r = —0.87).
( Development) Low Tide — Determinate larval abnormalities In
Liberty Bay waters collected during low tide ranged from 0.4% at several
stations to a high of 3.1% in surface waters from Station WSF—3 near the
95
-------
I
SAMPLE SITE
SURFACE
MID DEPTH
BOTTOM
0 500 1000
SCALE IN YARDS
Figure 30.
Relative per cent survival of Pacific oyster embryos in Liberty Bay waters
collected during high tide.
REFERENCE STATIONS
Il UOLi LANA! MISFHY P1
CL AM KAY 101
• r i
77 r
92 4
811
96
-------
Table 15. Pacific Oyster Embryo Responses as Related to Total Organic Carbon Levels in Liberty Bay Waters .
Tidal Depth Total Organic Mean Per Cent Mean Per Cent
Stations Stage (ni) Carbon (mg/l) Abnormal Larvae Relative Larval Survival
rty Bay Stations
0 9.0 3.1 71.5
WS -3 Low 3 2.0 0.4 88.3
(Near Poulsijo STP 6 3.0 0.8 90.7
Outfall)
High 0 16.0 6.4 41.6
5 3.0 0.8 99.9
9 3.0 0.3 100
WSF-5 Low 0 4.0 1.7 104
(Oyster Hatchery 3 3.0 1.3 89.8
Site) 6 3.0 0.4 94.8
High 0 17.0 95.8 20.2
5 2.0 0.7 97.9
9 2.0 0.0 89.8
WS-7 Low 0 50.0 - 0.0
(Mid-Bay) 3 3.0 1.1 61.6
6 3.0 0.4 94.5
High 0 0.7 77.5
5 1.1 92.4
9 0.2 81.1
Low 0 2.0 0.4 85.2
5 3.0 1.1 98.4
9 3.0 1.4 96.7
High 0 4.0 25.3 79.6
6 2.0 0.8 83.5
12 2.0 1.3 91.5
WSF-13 Low 0 3.0 0.5 100
(Iceyport STP 6 3.0 0.7 101
OUtfall) 12 3.0 0.6 89.7
High 0 4.4 96.3
7 2.9 83.7
14 0.7 99.4
f’ei ence Stations
HOOd Canal Low 0 0.8 105
(Misery Point) 3 1.1 92.9
6 1.2 101
CJ Bay Low 0 0.7 105
5 0.5 101
10 0.4 94.1
Relative to survival in Clam Bay (bioassay control) seawater
b Carry along control: 0.5% abnormality; 94.5% survival
97
-------
Scandi
SAMPLE SITE
* 100% MORTALITY
0 500 1000
SCALE IN YARDS
Pigure 31.
Per cent abnormal development of Pacific oyster embryos in Liberty Bay
waters collected during low tide.
REFERENCE STATIONS
HOOD CANAL ) MISERY PT,) 0.8
11
12
CLAM BAY 0 7
05
0.4
SURFACE
MID DE PT H
BOTTOM
98
-------
Poulsbo STP outfall. No mean percent abnormal larvae could be calcu-
lated for Station WS—7 surface waters, however, because of the complete
mortality that occurred in these samples. Although this mortality
certainly raised questions about the quality of water in the central
Bay (Station WS—7), all the determinate abnormality values were well
below Woelkets (1972) proposed single sample receiving water quality
criterion of 20% abnormality, as well as his multiple sample criterion
of 5% abnormality.
High Tide — The changes in larval abnormality observed between
low and high tide generally paralleled the tide—related changes in
larval survival described earlier. Larval abnormalities in waters
collected from the lower Bay during high tide increased substantially,
particularly in the surface waters from Station W—l1, in which 25.3%
abnormality was observed. Larval abnormality observed in surface
waters from Station WSF—3 increased slightly from 3.1% to 6.4%, while
abnormality in surface waters from Station WSF—5 rose from 1.7% to
95.8%. These changes were associated with a marked improvement in
surface water quality at Station W—7.
Just as in the case of larval survival, the presence or absence
of algal bloom conditions appeared to have a distinct influence on the
outcome of larval development. Although the cause of the increase in
larval abnormality at Station W—ll was not entirely understood, TOC
levels were positively correlated with larval abnormality during both
tidal stages studied (r 0.70).
Sediment
The bioassay of Liberty Bay sediments using Clam ay seawater as
99
-------
Scandu
SAMPLE SITE
E I E 1
MID DEPTH I
0 500 1Q00
SCALE IN YARDS
Figure 32.
Per cent abnormal development of Pacific oyster embryos in Liberty Bay
waters collected during high tide.
REFERENCE STATIONS
HOOD CANAL ) MISERY PT) 0 8
1.1
CLAM8AY1 37 12
Ob
0.4
100
-------
the diluent provided information on the relative toxicities of the
various sediments tested. The effects observed, however, did not nec-
essarily reflect the effects that would have occurred had the sediments
been diluted with Liberty Bay seawater.
Pacific oyster embryo response to surface sediments from Liberty
Bay, Clam Bay, and Hood Canal is shown in Table 16. The effect of
Liberty Bay sediments on larval survival was considered to be minor
considering the 85 — 99% survival observed at sediment concentrations
of 10 g/l. These sediments were also found-to have only a limited
effect on oyster embryo development. Most larval abnormalities occur-
ring in the 10 g/l sediment concentrations ranged from 1.1 — 2.5%,
while 15.3% abnormality was associated with surface sediments from
central Liberty Bay (Station WS—7). This high value exceeded the upper
range of abnormalities associated with (10 g/l) surface sediments from
Clam Bay and Hood Canal. Based on data collected by Schink, Westley,
and Woelke (1974) using a modified oyster embryo assay technique,
sediment core composites from Grays Harbor, Bellingham Bay, Henderson
Inlet, Pt. Whitney Lagoon, and the Duwamish River appeared to be con-
siderably more toxic to oyster embryos, however, than were the surface
sediments from Station WS—7.
Correlation analysis performed by Schink and his associates (1974)
indicated that the total suif ides concentration was the variable most
strongly correlated with the response of larvae to the core composites
they assayed. Total sulf ides, zinc, sediment particle size, BOD, and
total phosphorus were also found, by step—wise multiple regression
analysis, to have accounted for 93% of the observed variation in larval
response. 101
-------
Table 16. Pacific Oyster Embryo Responses (48—Hour) to Seawater Suspensions of Liberty Bay Surface Sediments .
Sediment Concentrations a
g/l Mean % Mean %
Station (Wet Weight) (Dry Weight) Abnormal Larvae Relative Larval Survivaib
Liberty Bay Stations
WSF—3 10 4.4 2.5 98.0
(Near Poulsbo STP Outfall) 1.0 0.44 0.5 101
0.10 0.044 1.0 102
0.01 0.0044 1.0 99.6
WSF—5 10 3.4 1.1 91.9
(Oyster Hatchery Site) 1.0 0.34 0.6 97.0
0.10 0.034 0.4 96.9
0.01 0.0034 0.5 97.2
WS—7 10 4.4 15.3 88.8
(Central Bay) 1.0 0.44 0.7 96.5
H 0.10 0.044 0.6 111
0.01 0.0044 0.7 103
WSF—13 10 6.9 1.4 85.0
(Keyport STP Outfall) 1.0 0.69 0.3 109
0.10 0.069 1.4 100
0.01 0.0069 0.4 96.5
Reference Stations
Hood Canal 10 7.8 0.3 106
(Misery Point) 1.0 0.78 0.4 99.6
0.10 0.078 0.8 84.9
0.01 0.0078 0.6 94.6
Clam Bay 10 6.5 1.0 101
1.0 0.65 0.5 101
0.10 0.065 0.2 90.2
0.01 0.0065 0.7 99.1
a Clam Bay (Bioassay Control) seawater used as diluent.
si tex
-------
The dry weight equivalent concentrations of total suif ides, metals,
and total volatile solids present in each 10 gIl (wet weight) Liberty
Bay sediment concentration assayed are presented in Table 17. Sediment
concentrations as high as 10 g/l (wet weight) would usually only be
associated with dredging or spoil disposal operations. This concentra-
tion was selected for inclusion in Table 17, however, because it was
the only concentration that, in some cases, appeared to adversely affect
larval response. Comparison of the various parameters listed failed
to reveal the positive correlation between total suif Ides and oyster
embryo response reported by others. Although higher concentrations of
total volatile solids were definitely associated with increased larval
abnormalities, a better understanding of the Individual and combined
effects of sulf Ides, volatile solids, metals, and other sediment para-
meters on embryo development and survival can only be obtained by
further study.
Sewage Treatment Plant Effluents
The acute toxicities of treated effluent composites collected 9—15
and 16—76 from the Poulabo, Keyport, and Torpedo Station STPs are listed
in Table 18. As in the case of the sediment bloassays, the toxicities
of the effluents diluted with Clam Bay seawater were believed to approx-
imate, but not necessarily duplicate, effluent toxicities in Liberty
Bay seawater.
The relative toxicities of the various STP effluents tested fol—
lowed the order: Poulsbo > Torpedo Station > Keyport. Waste discharge
from the Poulsbo plant was most toxic from the standpoint of both larval
103
-------
?.ABLg 17. Pacific Oyster Fzthryo
Responses (
48—Hour) Associated
with
Actual Concentrations of Metals, Total
Sulfides,
and Total
Volatile Solids
Contributed
by 10 gIl
(Wet weight) Sediment
Treatments.
concentration (ugh)
Oyster
obryo Response
Mean 8 - Relati4 ’
Larval Survival
station
Ant1
(Sb)
Arsenic
(As)
Cadmium
(Cd)
ctu’rgiiuni Copper
(Cr) (Cu)
Iron
(Fe)
Lead
(Pb)
Menganese
(Mi)
Mercury
(Hg)
Nickel
(Ni)
Zinc
(Zn)
Total SuJ.fides
Total Volatile
Solids (g/l)
Mean
Abnormal Larvae
Liberty B y Stations
F.-3
(Near Poulsbo SIP Outfall)
0.88
35
12
150 130
79,000
79
750
0.48
220
290
1600
0.21 g
2.5
98.0
WSF- 5
(Oyster Hatchery Site)
<0.34
37
44
180 220
110,000
320
1100
0.61
370
820
4400
0.24 g
1.1
91.9
_7
(Central y)
<0.44
57
16
200 200
120,000
200
1100
0.70
280
530
1400
0.34 g
15.3
88.8
P—13
(Ke ’pos .t STP Outfall)
<0.69
35
12
150 90
83,000
160
760
0.53
160
360
2300
0.21 g
1.4
85.0
Reference Stations
Hood Canal
(Misery Point)
‘0.78
55
9.4
220 160
140,000
47
3800
0.20
400
420
299
0.09 g
0.3
106
Clam Bay
23
39
6.5
140 140
78,000
200
680
0.63
120
650
600
0.11 g
1.0
101
0
-------
TABLE 18. Pacific Oyster Embryo Responses (48 Hour) to Treated Effluents from
Three Sewage Treatment Plants Discharging into Liberty Bay or
Nearby Waters.
Source of Treated Approximate Approximate
Effluenta EC5Ob (mill) LC5O° (mi/i)
Poulsbo STP 20 25 -50
Navy Torpedo Station STP 45 > 200
Keyport STP 140 > 200
a Clam Bay (Bioassay Control) seawater used as diluent
b Concentration of effluent resulting in 50% larval abnormality
o Concentration of effluent resuLting in 50% larval mortality
105
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abnormality and lethality. The approximate 48—hour EC5Oa and LC 5 Ob of
this waste were 20 mi/i and 25—50 mI/i, respectively. Treated effluent
from the Torpedo Station STP was characterized by an EC5O of 45 mi/l,
while the EC5O of the Keyport STP effluent was 140 mi/i. Both the
Torpedo Station and Keyport STP discharges were characterized by an
indeterminately high LC5O of >200 mi/i.
Comparison of the effluent EC5O and LC5O values with respect to
flow are presented in Table 19 for the purpose of showing the potential
acute toxic impacts of the STP effluents on the Liberty Bay system.
The Poulsbo STP had the greatest potential toxic impact, discharging
53.0 io 6 EC5O units or 21.2 x i0 6 — 42.4 x io 6 LC5O units per day.
Least potentially toxic was the Keyport STP effluent. The daily dis-
charge from this facility was <0.541 x io6 EC5O units or <0.379 x io 6
LC5O units. The Torpedo Station effluent was intermediate in potential
toxicity, discharging 9.24 x io 6 EC5O units or <2.08 x 106 LC5O units
per day to the Liberty Bay system.
Biological Significance of Various Chemical and Biological Factors —
The cause(s) of the recurrent mortalities of Pacific oyster embryos
and larvae reported by Sea Farms, Inc. was not definitely determined.
Several factors were identif led, however, that alone or in combination
with each other, may have contributed to the Sea Farms problem. These
factors included algal blooms, sewage treatment plant effluents, suif ides,
aEC5 O — Concentration of effluent resulting in 507 larval abnormality
bLC5O — Concentration of effluent resulting in 50% larval mortality
106
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TABLE 19.
Estimated Number of Acute Toxic Units Discharged Daily to
Treatment Plants
(MGD)
(mi/day)
0.28
10.6 X i0 8
0.11
4.16 X io 8
O.O2
0.757 X io8
Approximate EC5O’°
(‘ni/i)
EC5O Units Disc harged
Per Day
LC5O Units Discharged
Per Day
25—50
45
a Estimated
b Based
EC 50
LC5O
on 48-Hour Oyster Embryo Assay
Concentration of effluent resulting in 50% larval abnormality
Concentration of effluent resulting in 50% larval mortality
Flow:
Sewage Treatment Plant
Parameter Poulsbo — Thrpedo tI ion - — Keyport
the Liberty Bay System by Local Sewage
0
—4
20
b
Approximate LCSO
(mi/i)
140
53.0
X
i0 6
9.24 X 106
0.541
X
io 6
>200
>200
21.2
X
106_42.4 x i 6 <2.08 X 106
<0.379
X
106
-------
total volatile solids, untreated plating wastes, metal laden sediments,
and PBI—sensitive substances. The possible biological significance of
some of these factors has already been presented; others are discussed
in more detail below.
Mercury
No major sources of mercury or evidence of serious mercury contam-
ination were found during the survey. Consequently, excessive mercury
concentrations in Liberty Bay waters did not appear to be a probable
cause of the mortality problems experienced by Sea Farms, Inc. The
report of mercury levels in Liberty Bay as high as 110 ugh could not
be substantiated. Any evidence confirming this report would have been
very significant. The acute toxicity of mercury (as IigCl) to Pacific
oyster embryos was reported to be 32 ug/]. (Okubo and Okubo, 1962). More
recently, Calabrese and Nelson (1974) observed a 50% mortality of embryos
of American oysters, C. virginica , and hard clams, Mercenaria mercenaria ,
in 48 hours at mercury concentrations of only 5.6 ugh and 4.8 ugh,
respectively.
When relating these acute toxicity data, as well as the other 48—
hour bioassay results presented in this report, to the Sea Farms problem
it should be understood that most of the mortalities reported by Sea
Farms occurred a week or more following spawning. This does not neces-
sarily mean that exposure periods of a week or more were involved. How-
ever, had the experimental bioassay protocols included similar exposure
periods, the toxicities of the various agents tested would have appeared
even greater since less material would most likely have been required to
produce the effects originally observed at the end of 48 hours.
108
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Other Metals
Because of the analytical problems encountered during the seawater
metals analyses, it was not possible to assess the biological signifi—
carice of other metals levels in Liberty Bay seawater. It was possible,
however, to estimate the seawater metals concentrations that could have
occurred in Liberty Bay following continuous and intermittent bypasses
of metallic plating wastes from the Torpedo Station (Table 20). These
estimates were made using the following formulas:
( Continuous Discharge )
Under the conditions described below, the steady state concentra-
tion, Cs, in Liberty Bay is given by:
C 5 Q x w
Qtide
where:
Qw = waste flow c.f.s.
Cw = waste concentration, mg/i
Qtide = tidal exchange rate, c.f.s.
c ____
50,000
Assumptions,
1. Entire portion of Liberty Bay is completely well mixed
during one tidal cycle.
2. Water coming in on a flood tide carries no residual
from the previous ebb.
3. Only inflow to Liberty Bay is from waste discharge.
4. Waste flow rate is 3141 GPH.
109
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Table 20. Estimated Total Metal Concentrations in Liberty Bay Seawater Result:ing from
Bypassing Plating Wastes at the Navy Torpedo Station, Keyport, Washington.
Concentration ugh
Possible
Background Total
Metal Concentrations
in Seawatera (ugh )
0.08
0.3
1.1
1.2
4.3
6.2
Suggested Hazardous
Total Metal Concentration
in Seawaterb (ugh)
>10
>10
>50
>50
>0.10
>100
>100
a Source: Davey and Soper, 1975 (Narragansett Bay)
b Source: National Academy of Sciences, Water Quality Criteria, 1972
C Concentrations in upper 3—meter water column at Sea Farms Hatchery site
d Concentrations throughout Liberty Bay
Intermitten BypassC
Element
Cadmium (Cd)
Chromium (Cr)
Copper (Cu)
Lead (Pb)
I-I
Mercury (Hg)
Nickel (Ni)
Zinc (Zn)
2—Hour Duration
Flow Rate (GPII)
Continuous Bypassd
Flow Rate (GPH)
(3141)
(2082) (197)
(3141)
(2082) (167)
0.26
0.20 0.09
0.22
0.17 0.09
1.1
0.80 0.34
0.87
0.68 0.33
1.1
1.1 1.1
1.1
1.1 1.1
1.2
1.2 1.2
1.2
1.2 1.2
0.1
0.1 0.1
0.1
0.1 0.1
7.8
6.6 4.5
7.0
6.1 4.4
-------
5. Tidal amplitude is 6 feet.
6. Surface area of Liberty Bay is 0.45 x io8 square feet.
7. Tidal period is 12.4 hours.
( IntermIttent Discharge )
Under the conditions described below, the concentration, C, for
an intermittent discharge during the time t=o to t=t, at some point, x,
downstream from the discharge is:
—{x--u(t T)}2
Q *io 6 ( i 1
C = A (4 3½ ) F—T e 4K(t 1 —T) dT
to 1
where:
= mass loading rate, lbs/sec
A = cross—sectioned area at point of discharge, square feet
p = density of discharge, lbs/ft 3
K = diffusion coefficient, ft 2 /sec
u = velocity of receiving water, feet/sec
during time variable, seconds
x = longitudinal distance downstream, feet
Assumptions,
1. Well mixed vertically over a depth of 3.0 meters.
2. Lateral boundaries do not influence diffusion or disper-
sion processes.
Calculations were made using the highest metal concentrations meas-
ured in the plating plant sump or plating treatment plant effluent during
the Compliance Monitoring Inspection (EPA, 1975). The flow rates on
which the estimates were based represented the highest, median, and
ill
-------
lowest flows of bypassed plating waste actually measured by the Navy
during 16 bypasses reported from March 10, 1975 to September 17, 1975.
For purposes of comparison, Table 20 also includes the hazardous metal
concentrations suggested by the National Academy of Sciences (1972) for
oyster growing waters. Most of the background total metals levels used
in the calculations were based on the analysis of Narragansett Bay sea-
water (Davey and Soper, 1975). These levels were generally similar,
however, to unpublished total metal Concentrations recently measured
in Puget Sound by other investigators (Personal Communication, Dick
Huntamer, Seattle, WA).
Under the worst possible conditions, characterized by the strati-
fied dilution of an intermittent 3141 GPH bypass, none of the estimated
individual metal concentrations exceeded suggested hazardous levels at
the Sea Farms hatchery site. The combined effect of these estimated
metal concentrations was evaluated by determining whether or not they
exceeded a hazardous level defined by the formula presented below
(National Academy of ScIences, 1972).
C Cb Cn
+ — + •.. + < 1.0 (Hazardous Concentration)
La Lb
where:
C = Estimated concentrations following Intermittent 2—hour
bypass (3141 GPH)
L = Suggested hazardous levels not to be exceeded
Although this application of the formula exceeded its intended use, the
results suggested that the combined contributions of metals would also
112
-------
not have exceeded a hazardous level by the time they reached the Sea
Farms site.
It is important to note that many of the hazardous levels suggested
bythe National Academy of Sciences were found to be in reasonable agree-
ment with metal concentrations estimated to be safe for oyster embryos
of the genus Crassostrea (Table 21). The estimated “safe” concentrations
were generated by multiplying known 48—hour LC5O values by an appropriate
application factor (ratio of safe to lethal concentrations) suggested by
the Academy (1972).
Sewage Treatment Plant Effluents
The bioassay of the STP effluents provided information on the rela-
tive toxicities of the treated wastes as described earlier. By applying
appropriate application factors (safety factors) to these data it was
possible to also estimate the “safe” dilutions of the various wastes and
compare these values with the minimum dilutions of the wastes estimated
to occur at a point 1000 meters from their source (Table 22). This
technique provided a means of assessing the potential impact of the
STP effluents on the Sea Farms hatchery operation under a variety of
realistic tidal speeds and diffusion rates.
Estimates of the minimum waste dilutions were computed by the use
of the following formula (Pearson, 1961):
Smin = 3.64 D u y x
Q
where:
D = water depth, meters
113
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Table 21. Estimated Safe Concentrations of Various Metals to Oyster Embryos of the Genus Crassostrea .
a Source: National Academy of Sciences (1972)
b Concentration resulting in 50% larval abnormality
c Concentration resulting in 50% larval mortality
d Assigned
Suggested Application
Element Factora
4b 8 _Hour
ECSO or LC5OC
(ug/l) Species
Estimated Safe
Concentration
(Factor X 48-Hr.
Reference EC5O or LCSO)(ug/l)
Suggested
Hazardous
Concen—
tration(ug/1)
Arsenic (As)
Cadmium (Cd)
0.01
0.01
7500
920 b
3800
Crassostreavirginica
Calabrese et.
(Cardwell et.
(Calabrese et.
al.,1973)
al., In prep.)
al., 1973)
75
9.2
38
>50
>10
C.
C.
gigas
virginica
Chromium (Cr)
0.0].
10300
C.
virginica
T
103
>10
Copper (Cu)
0.01
103
C.
virginica
“
1.0
>50
Lead (Pb)
0.02
2450
C.
virginica
“
24.5
>50
Manganese (Ma)
0.02
16000
C.
virginica
“
320
>100
Mercury (Hg)
001 d
5 ’
C.
virginica
F,
0.06
>0.1
a
. -
Nickel (Ni)
Zinc (Zn)
0.02
0.01
1180
310
C.
C.
virginica
virginica
r
TT
23.6
3.1
>100
>100
-------
Table 22. Estimated Minimum Dilution of Sewage Treatment Plant Effluents
1000 Meters from Their Source Under Different Tidal Speeds and Diffusion Rates
Estimated Minimum DilUt Ofla
Diffusion Coefficientb (m 2 /second )
Effluent Source Approximate o.i 1.0
(Distance from Sea Farms ECSO Application Estimated
Hatchery Site, meters) (DilUtlOfla) Factore Safe Dilutiona (Tidal Sveedb (rn/second)) (Tidal Speedb (n/second))
(5.79 X l0— ) (2.04 X 10-1) (5.79 X 10-2) (2.04 X 10—i-)
0.01 (1/100) 5,00G
Poulabo STP 50 0.05 (1/20) 1,000 1,070 2,010 1,850 3,480
(870)
(1.00 x 10_i) (6.71 X 10_i) (1.00 X lo_l) (6.71 X 10_i)
Na To edo 0.01 (1/100) 2,200 7,000 18,000 12,100 31,100
Station STP 22
(2510) 0.05 (1/20) 440
(1.00 X 10_i) (6.71 X 10_i) (1.00 X 10_i) (6.71 X 10_i)
Keyport STP
0.01 (1/100) 700 60,000 100,000 100,000 100,000
(2560) 0.05 (1/20) 140
aDilutions presented as 1:X
bSoi,u .ce: Roats Engineering, 1970
CSoijrce: National Acaden r of Sciences, Water Quality Criteria, 1972.
-------
y = lateral coefficient of eddy diffusivity, meters 2 /second
u longitudinal speed of advections, meters/second
Q = waste discharge rate, meters 3 /second
x = longitudinal distance downstream, meters
Assumptions,
1. Steady state horizontal diffusion and advection processes
are the primary mechanisms dispersing the waste during a
tidal cycle.
2. Wastes are mixed uniformly over a depth of 3 meters at
the surface. The thickness of this layer does not change
even though water depth increases.
3. Horizontal advection speeds can be obtained from float
studies performed during 1964 and 1970 by Roats Engineer-
ing, Poulsbo, Washington (1970).
Based on these estimates, treated discharges from the Torpedo Sta-
tion and Keyport STPs would have been sufficiently diluted at a point
less than halfway to the hatchery site to be considered safe for expo-
sure to Pacific oyster embryos regardless of the tidal speed, diffusion
rate, or inherent safety of the application factor applied. Using the
smallest application factor presented (0.05; 1/20), effluent from the
Poulsbo STP would have been diluted enough 1000 meters from the outfall
to be considered safe for exposure to oyster embryos. The fact that
the outfall was only 870 meters up—Bay from the Sea Farms site raises
some questions, however, about the adequacy of the dilution, particu—
larly at lower tidal speeds.
Although the application of a safety factor of 0.05 (1/20) to STP
effluents is not unreasonable, the National Academy of Sciences (1972)
suggested applying factors of 0.01 (1/100) and 0.02 (1/50) to most of
116
-------
the potentially toxic constituents, primarily metals, found in the
treated wastes being discharged to Liberty Bay. Assessments of the
potential impact of these wastes should, therefore, at least be based
on safety factors that are consistent with the most toxic constituents
present. Consequently, the application of a safety factor of 0.01
(1/100) to the Poulsbo STP effluent indicated that under certain
conditions these wastes would not have been significantly diluted by
the time they reached the Sea Farms site to be considered “safe t ’ for
oyster embryos.
The fact that estimated dilutions of treated wastes from the
Poulsbo STP did not, in every case, exceed the dilutions of this
effluent estimated to be safe to oyster embryos certainly does not
establish the Poulsbo STP as being the sole source of Sea Farms’
problems. It does suggest, however, that these treated wastes may
have contributed, at one time or another, to the reported mortalities
of oyster embryos and larvae.
Phytoplankton, Bacteria, and Fungi —
Undefined conditions associated with the dense phytoplankton popu-
lations that were present in east—central Liberty Bay during the survey
(September 15, 1976) appeared to have adversely affected the laboratory
development and survival of Pacific oyster embryos more than any other
factor. Although it was not determined what agent or which organism
was responsible for the poor embryo response, the dinoflagellates, as
well as associated bacteria and fungi were considered to be likely
candidates.
117
-------
Several marine dinoflagellates have been shown to produce potent
toxins capable of adversely affecting a variety of organisms (Sasner,
1973). For example, the toxin(s) produced by the marine dinoflagellate,
Gymnodinium breve , has been directly responsible for massive mortal-
ities of marine organisms in the Gulf of Mexico (Davis, 1948), while
a number of human illnesses and deaths have occurred along the Pacific
and Atlantic coasts of the United States as a result of the consumption
of molluscs containing paralytic shellfish poison (PSP) produced by
the dinoflagellates Gonyaulax catenella and G. tamarensis , respectively
(McFarren at al., 1956). Halstead (1965) also suspected several other
dinoflagellates as producing substances that were potentially toxic to
man as well as marine organisms. Interestingly, the list of suspect
dinoflagellates included the dinoflagellate, Gymnodinium splendens ,
and members of the genus, Prorocentrum ——— both of which were the
predominate dinoflagellates identified in the Liberty Bay algal bloom.
In addition to the potentially harmful impact of blooms of toxigenic
algae, algal blooms have also created adverse conditions as a result
of nutrient imbalance, oxygen deficiency, and hydrogen sulfide pro-
duction resulting from the decomposition of organic matter and the
presence of increased numbers of bacteria (Sasner, 1973).
Although algal blooms have not been directly implicated in pre-
vious mortalities of Pacific oyster embryos and larvae, the adverse
effect of certain algae, bacteria, and fungi on the early life stages
of several other marine bivalve molluscs has been well documented.
Davis and Guillard (1958) observed the green alga, Stichococcus sp .,
and the brackish water golden alga, Prymnesium parvum , to be toxic
118
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to the larvae of American oysters, C. virginica and hard clams,
M. mercenaria , when supplied as food. One of the earliest records
of bacteria exerting a harmful effect on oyster larvae was that of
Davis (1953) who found that bacteria affected both the growth and
survival of larvae of the American oyster. Similar observations
were made by Walne (1958) using larvae of the European flat oyster,
Ostrea edulis , and by Guillard (1959) who found isolates of the bac—
teria Vibrio sp. and Pseudomonas sp. to be harmful to larvae of hard
clams. Davis (1954) also determined that the fungus, Sirol idium
zoophthoruin , was responsible for the extensive mortality of clam larvae
being reared in the laboratory.
Several antibiotics were demonstrated to effectively reduce the
harmful effects of certain bacteria and fungi on bivalve larvae. It
is significant, however, that as early as 1955, Loosanoff and Davis
(1963) found it necessary to treat all seawater and algal food supplies
used in the cultivation of bivalve molluscs with ultraviolet (UV)
light to reduce the potential adverse impact of associated bacterial
and fungal populations. Later, Sinderman and Rosenfield (1967) pro-
posed that disease—related mortalities of Invertebrates under cultiva-
tion be controlled by a combination of UV and antibiotic treatment of
filtered seawater coupled with good sanitation practices, the control
of contaminants In algal cultures, and the elimination of intermediate
disease hosts.
Before Sea Farms, Inc. closed Its oyster hatchery as a result of
excessive larval mortalities it had been using a sand filter to remove
the larger materials from its incoming seawater supply. It had also
119
-------
applied various antibiotics in an unsuccessful attempt to control the
mortalities. Ultraviolet light had not been used, however, to treat
its incoming seawater supply or the algal cultures being fed to the
larvae under cultivation. Contamination of the larval cultures with
ciliate protozoans (peritrichs) known to feed on bacteria was also
observed on occasion (Personal Communication, Sea Farms, Inc.).
Marine water quality information collected by the Washington
State Department of Fisheries Indicates that potential oyster larvae
abnormality and mortality problems are not necessarily limited to
Liberty Bay or the Sea Farms operation. In the early 1960s concern
grew over the increased mortalities of commercially important Pacific
oysters in Washington State waters. Westley etal., (1966) reported
that natural mortalities of adult Pacific oysters in southern Puget
Sound appeared to be associated in some way with fall blooms of the
armored dinoflagellate, Ceratium . A similar observation was made by
Scholz, Westley, and Tarr (1968). Unable to establish a definite cause
and effect relationship, Westley and his associates (1966) recognized
the possibility that the organism responsible for the adult mortalities
may not have been Ceratium , but some other organism associated with
blooms of this alga. More recently, bacteria associated with warm,
nutrient—rich waters have been implicated as the cause of these mor-
talities (Lipovsky and Chew, 1974; Grischkowsky and Liston, 1974).
In conjunction with their work on adult oysters, Westley etal,,
(1966) also performed oyster embryo assays on selected waters from
southern Puget Sound and Hood Canal to determine if oyster embryo
response (as measured by embryo development) could be related to the
120
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adult mortalities. Larval abnormality was not found to be significantly
related to adult mortality, salinity, P31—sensitive substances, or
chlorophyll a. An unexplained decline in some of the larval populations
did appear to occur, however, during the 48—hour test period. These
population reductions may have resulted from the accidental mechanical
loss of individuals during bioassay termination as shown to be possible
by Cardwell etal., (In preparation). It is also possible, however,
that the decline in the numbers of larvae actually reflected larval
mortalities that may have been related to conditions associated with
algal blooms and the deaths of the adult oysters.
Long—term water quality monitoring by the Department of Fisheries
has tended to support the latter possibility. Occasional increases in
larval abnormality and mortality rates have been observed in the pro-
ductive southern Puget Sound waters In question (Eld, Totten, and Budd
Inlets) as well as in waters from southeastern Flood Canal, Carr Point,
and from Discovery Bay located between the Strait of Juan de Fuca and
Admiralty Inlet. The poor embryo or larval responses observed are
believed to have been directly related to the microbial populations of
the waters tested (Personal Communication, Rick Cardwell, Washington
State Department of Fisheries, Brinnon, WA).
Liberty Bay waters assayed by Department of Fisheries personnel
from 1962—1975 were characterized by relatively good larval develop—
merit. Intermittent larval mortalities were observed, however, in
surface waters collected near the City of Poulsbo (Personal Comrnunica—
don, Rick Cardwell, Washington State Department of Fisheries, Brinnon,
WA). Although the cause of these mortalities was not established, they
121
-------
demonstrate that, at times, certain Liberty Bay waters have been unsuit-
able for rearing the early life stages of Pacific oysters.
The background information presented above certainly suggests that
toxic microbial metabolites or infectious diseases may have contributed
substantially to the oyster embryo and larvae mortalities experienced
by Sea Farms, Inc. Further investigation would be required, however,
to confirm or refute this possibility.
122
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126
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127
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APPENDIX A
128
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State of Washington, Department of
Ecology Standards for Class AA
(Extraordinary) Water Quality
(State of Washington, 1973).
(1) Class AA (Extraordinary) .
(a) General characteristic. Water quality of this class shall
markedly and uniformly exceed the requirements for all or substantially
all uses.
(b) Characteristic uses. Characteristic uses shall include, but
are not limited to the following:
(1) Water supply (domestic, industrial, agricultural).
(ii) Wildlife habitat, stock watering.
(iii) General recreation and aesthetic enjoyment (picnicking,
hiking, fishing, swimming, skiing, and boating).
(iv) General marine recreation and navigation.
(v) Fish and shellfish reproduction, rearing, and harvest.
(c) Water quality criteria.
(i) Total coliforin organisms shall not exceed median values of
50 (fresh water) or 70 (marine water) with less than 10% of samples
exceeding 230 when associated with any fecal source.
(ii) Dissolved oxygen shall exceed 9.5 mg/l (fresh water) or
7.0 mg/i (marine water).
(iii) Total dissolved gas — the concentration of total dissolved
gas shall not exceed 110% of saturation at any point of sample collection.
(iv) Temperature — water temperatures shall not exceed 600 F.
(fresh water) or 550 F. (marine water) due in part to measurable (0.50 F.)
increases resulting from human activities; nor shall such temperature
increases, at any time, exceed t = 75/(T—22) (fresh water) or t 24/
(T—39) (marine water); for purposes hereof “t” represents the permissive
increase and “T” represents the water temperature due to all causes com-
bined.
(v) j shall be within the range of 6.5 to 8.5 (fresh water) or
7.0 to 8.5 (marine water) with an induced variation of less than 0.1
units.
129
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(vi) Turbidity shall not exceed 5 JTU over natural conditions.
(vii) Toxic, radioactive, or deleterious material concentra-
tions shall be less than those which may affect public health, the
natural aquatic environment, or the desirability of the water for
any usage.
(viii) Aesthetic values shall not be impaired by the presence
of materials or their effects, excluding those of natural origin,
which offend the senses of sight, smell, touch or taste.
130
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APPENDIX B
131
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Pou lsbo
lbs/d
0.25 MGDa
1169
242
Parameter
Flow
Total Solids
Total Suspended
Solids
Total Dissolved
Solids
to 9—19—75)
Relative Point Source Loadings to Liberty Bay (9-15-75
Sewage Treatment Plants
_____________________ Keyport _______ _______
lbs/d _______________ ________
71 .02 MGD 6
69 88.5 5
82 5.33 2
t—
Torpedo
lbs/d
0.08 MGD
442
48
Station
23
26
16
894 68 68 5 352
Total
Colifornis
1100/100 ml - <18/100 nil 4600/100 ml
12.6
0.07
Total
Phosphorus
26.3
4.13
Ammonia Nitrogen
52.08
6.27
Total
load (lbs/d)
0.35
1700
295
1314
12.69
32.65
58.5
Total Metals
Cd
Cr
99
81
89
12
3
0.02
2.22
0.117
0. 0018
0.0013
0. 0116
0. 0279
*
C
0
0
z
z
z
-I
z
6)
0
1,
1,
n
In
4
-J
0
‘0
0
a
1. 1
-a
0
In
0
0
z
0
27
0.6
13
11
87
97
100
45
28
52
97
0.2
7
0.2
2
0.1
7
4
2
0.1
15
Hex Cr.
Cu 0.0792 48 0.0115
Pb 0.0815 68 0.005
Hg 0.0007 46 0.000033
Ni 0.198 3 0.0042
Zn 0.442 56 0.117
a MGD - million gallons per da y
b - ineth jlene blue active substances
0.0868
0.1
0.994
1.023
0. 0199
0.0749
0.166
0.0342
0.121
0.0008
0.002
5.95
6.15
0.227 29
0.786
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