NORTHWEST ENVIRONMENTAL CONSULTANTS, INC.
158 Thomas Street, Suite 32
Seattle, Washington 98109
HISTORY AND EFFECT OF PULPMILL
EFFLUENT DISCHARGES,
BELLINGHAM, WASHINGTON
FINAL REPORT
May 1981
By :
G. Bradford Shea - Project Director (NEC)
Curtis C. Ebbesmeyer (EHI)
Quentin J. Stober (UW)
Kathy Pazera (NEC)
Jeffrey M. Cox (EHI)
Susan Hemingway (NEC)
Jonathan M. Helseth (EHI)
Laurence R. Hinchey (EHI)
Submitted to;
U.S. DEPARTMENT OF JUSTICE, and
U.S. ENVIRONMENTAL PROTECTION AGENCY
-------
ACKNOWLEDGEMENTS
Many people contributed to the success of this project. Several
In-house staff personnel contributed vital efforts. Mari Goodrich
typed and proofed the entire manuscript, including innumerable
drafts. John Hoge and Diane Koran prepared the graprhic illustra-
tions at NEC. Evans Hamilton production staff included David
Browning (data compilation), Carol Coomes (typing,data compilation)
and Terry Storms (graphics).
The authors wish to thank Jim Moore (Department of Justice) and
Tom Waite (Environmental Protection Agency) for encouragement
and support throughout the project. John Yearsley assisted with
logistical support, especially on boat surveys of the area.
He and Richard Callaway (EPA) also helped locate important field
work. Many other EPA staff members supplied help and information
at various points during the project.
We also wish to express our thanks to the many other agency,
university and private personnel who supplied data or information.
In particular state (DOE, WDG, WDF) agencies were very helpful
in this report.
-i-
-------
MOTE ON UNITS AND ABBREVIATIONS
Metric units are used as the standard for this report. In many
cases, however, data.on effluents, fish, or other quantities is
uniformly, reported in English units. In these cases, we have
usually preserved the English units and, where convenient, have
placed the metric equivalent in parenthesis or at least given a
conversion factor.
iVbbreviations for commonly used words or phrases can be found
on the following page. One commonly confused quantity is the
term Sulfite Waste Liquor (SWL). This term is now commonly refer-
red to as Spent Sulfite Liquor (SSL) although the original data
sources often use SWL. In this report, we have uniformly used
SSL regardless of the data source, except in cases where a direct
quotation is involved.
-------
ABBREVIATIONS
ASB Aerated Stabilization Basin
BOD Biological Oxygen Demand
CGW Chemican Groundwood Plant
DMR Georgia-Pacific's Daily Monitoring Reports
DO Dissolved Oxygen
DOE Washington State Department of Ecology
EASB Estimated Adult Spawning Biomass
EHI Evans-Hamilton, Inc.
EIS Environmental Impact Statement
EPA United States Environmental Protection Agency
FAO United States Fish & Wildlife Service's Fisheries
Assistance Office
FRI Fisheries Research Institute
FWPCA Federal Water Pollution Control Administration
GP Georgia-Pacific Corporation
IRI Index of Relative Importance
MHHW Mean Higher High Water
MLLW Mean Lower Low Water
MSN Mathematical Sciences Northwest
NEC Northwest Environmental Consultants, Inc.
NOAA National Oceanic and Atmospheric Administration
NOS National Ocean Survey
NPDES National Pollutant Discharge Elimination System
NTU (turbidity)
PBI Pearl Benson Index
PCHB Pollution Control Hearings Board'
POP Platforms of Opportunity Program
PSTF Puget Sound Task Force
S Salinity
SCS Suspended Combustible Solids
SME Sulfite Mill Effluent
SP Scott Paper mill
SS Suspended Solids
SSL Spent Sulfite Liquor
STORET EPA's Water Quality Data Storage and Retrieval System
STP Sewage Treatment Plant
SWL Sulfite Waste Liquor
T Turbidity
TS Total Solids
TSS Total Suspended Solids
USCGS United States Coast and Geodetic Survey
USDI United States Department of the Interior
USGS United States Geological Survey
UW University of Washington
WDF Washington State Department of Fisheries
WDG Washington State Department of Game
WPCC Washington State Pollution Control Commission
WPT Water Treatment Plant
-iii-
-------
UNITS OF MEASUREMENT
adt average dry tons
mgd million gallons per day
mid million liters per day
ppm parts per million
ppt parts per thousand
-iv-
-------
CONTENTS
Page
Note on Units and Abbreviations . ii
List of Abbreviations ........ iii
Units of Measurement. . ¦ • . . . ". . . . iv
EXECUTIVE SUMMARY 1
I. HISTORY OF THE GEORGIA-PACIFIC PULP AND PAPER MILL AT
BELLINGHAM, WASHINGTON 4
A. Processes and Operations . 6
B. Permits and Regulations 17
C. Compliance History. 28
II. INDUSTRIAL AND MUNICIPAL EFFLUENTS AND COMPOSITION. . . .. 38
A. Effluent Discharges 38
B. Mill Closures 71
C. Effluent Composition and Toxicity . 73
III. OCEANOGRAPHIC DYNAMICS. 83
A. PHYSICAL AND GEOGRAPHIC CHARACTERISTICS 86
B. DATA SOURCES AND METHODS. 89
C. FLOW CHARACTERISTICS 98
D. WATER PROPERTIES. . 103
E. EFFLUENT DILUTION . 106
IV. WATER QUALITY 117
A. WATER QUALITY CRITERIA. ..... 117
B. WATER QUALITY MONITORING. 118
V. TOXICITY. 152
A. LITERATURE REVIEW OF SULFITE MILL EFFLUENT TOXICITY
B. GROSS TOXICITY BIOASSAYS 159
C. MAJOR EFFLUENT COMPOUNDS AND ORGANISM RESPONSE. . . 179
VI. BIOLOGICAL RESOURCES 199
A. PHYTOPLANKTON AND MACROPHYTES ........... 199
B. ZOOPLANKTON .210
C. SHELLFISH 218
D. OTHER INVERTEBRATES 221
E. FISH 239
F. WILDLIFE. . 268
-v-
-------
Page
VII. ECOLOGICAL EFFECTS T5IT
A. OVERVIEW 290
B. TROPHIC STRUCTURE. . ....... 292
C. DAMAGE MECHANISMS ..302
D. ECOSYSTEM EFFECTS ... ..... . . 304
E. SUMMARY 305
VIII. ANALYSIS AND RESULTS . . . .... . . 309
A. OCEANOGRAPHIC DYNAMICS 309
B. WATER QUALITY ¦.'.... 343
C. TOXICITY 352
D. BIOLOGICAL AND ECOLOGICAL. . . 374
IX. CONCLUSIONS . . 380
APPENDICES 382
-vi-
-------
LIST OF APPENDICES
Page
A. SUMMARY OF CURRENT METER MEASUREMENTS IN ROSARIO
STRAIT AND ROSARIO APPENDAGE AND OBSERVATIONS OF
DYE AND DRIFTING OBJECTS IN ROSARIO STRAIT AND
ROSARIO APPENDAGE. . ................ 383
B. OBSERVATIONS OF WATER PROPERTIES IN ROSARIO STRAIT
AND ROSARIO APPENDAGE 391
C. AERIAL AND SATTELITE PHOTOGRAPHS OF ROSARIO STRAIT
AND ROSARIO APPENDAGE. . 396
D. MONTHLY TEMPERATURE VERSUS SALINITY. ........ 398
E. ACUTE TOXICITY BIOASSAY TEST METHOD AND STATIC-BIOASSAY
TO EVALUATE INDUSTRIAL EFFLUENT TOXICITY 404
F. RECEIVING WATER BIOASSAY RESULTS AND SSL LEVELS. . . 411
G. PLANKTON DATA. . . 430
H. SPECIES LIST OF INVERTEBRATE ORGANISMS ....... 434
J. SHELLFISH BEDS 439
K. BEACH TRANSECTS: PROFILES 445
L. SAMPLING TRANSECTS AND LOCATIONS 452
M. STREAMBED AND FLOW CHARACTERISTICS OF THE NINE
DRAINAGES IN THE BELLINGHAM-SAMISH BASIN ...... 459
N. ANADROMOUS FISH ESCAPEMENTS AND CATCH RETURNS. ... 462
0. MARINE BIRD SPECIES 474
P. BIRD CENSUS METHODS 480
Q. SEASONAL PROJECTIONS OF BIRD DENSITY AND NUMBERS . . 482
R. GEOGRAPHICAL HABITAT TYPES USED BY BIRD SPECIES. . . 488
-vii-
-------
LIST OF FIGURES
Page
1-1. Location of the Georgia-Pacific Pulp and Paper Mill . 5
1-2. Outfalls of Georgia-Pacific, Bellingham Bay Inner
Harbor 10
1-3. "Schematic of Water Flow" for Georgia-Pacific . . . . 12
II-l. Washington State Department of Ecology Water Classi-
fications at Bellingham Bay 39
II-2. History of the Known Industrial and Municipal
Discharge Locations 43
II-3. Georgia-Pacific Average Monthly Effluent Flow .... 49
II-4. Georgia-Pacific Monthly Average for SCS ....... 51
II-5. Georgia-Pacific Monthly Average for TS. . 52
II-6. Georgia-Pacific Monthly Average for BOD 53
II-7. Georgia-Pacific Monthly Average for TSS ....... 55
II-8. Georgia-Pacific Monthly Average for SSL 56
II-9. Georgia-Pacific Chlorine Plant Monthly Average for
Mercury 58
11-10. Georgia-Pacific Chlorine Plant Monthly Average for
Chlorine 59
11-11. Discharge Locations from Bellingham STP and South
Bellingham. .. ........... 68
11-12. Post Point Treatment Plant and Outfall Location ... 69
III-l. Overview of Oceanographic Study Area. . . 84
III-2. Oceanographic Study Area 85
III-3. Bottom Contours in the Rosario Appendage 87
III-4. Boundaries of Bellingham, Samish, Fidalgo and Padilla
Bay Systems 91
III-5. Seasonal Progression of Prevailing Winds . 94
III-6. Annual Variations of Air Temperature, Wind, River
Runoff and Precipitation. . 95
III-7. Cross-Sectional Views of the Puget Sound-Strait of
Juan de Fuca-Strait of Georgia System 100
III-8. Pathway of Seabed Drifters Released off the Washington
and Oregon Coasts 101
III-9. Depth Profiles of Net Currents in Haro and Rosario
Straits, Entrance Channels to Rosario Appendage and
Bellingham Bay. 102
-viii-
-------
Page
111-10. Water Characteristics of Puget Sound and Associated
Estuaries. . . . 104
111-ll. Seasonal Cycles of Temperature, Salinity, Density
and Dissolved Oxygen 106
112-12. Seasonally Averaged Vertical Profiles. ....... 107
111-13. Vertical Profiles of Water Properties During Local
Periods of High and Low. River Flow 108
IV-1. Water Sampling Stations in the Bellingham Area ... 121
IV-2. Three Sampling Areas in the Bellingham-Samish Bay
System ... . . . . . ... . . . . . . . . 123
IV-3. Cumulative Percent Frequencies of SSL in Bellingham
Bay north of Post Point and Point Frances 124
IV-4. Cumulative Percent Frequencies of SSL between Post
Point and Governor's Point to Eliza Island 125
IV-5. Cumulative Percent Frequencies of Dissolved Oxygen . 126
IV-6a. Dissolved Oxygen Levels Recorded at Stations 1 & 5 . 127
IV-6b. Dissolved Oxygen Levels Recorded at Stations 3 & 3A. 128
IV-6c. Dissolved Oxygen Levels Recorded at Stations 15 &
17 ... 129
IV-7a. Time History of SSL Levels at Stations 1 & 5 . . . . 130
IV-7b. Time History of SSL Levels at Stations 3 & 3A. . . . 131
IV-7c. Time History of SSL Levels at Stations 15 & 17 . . . 132
IV-8. Surface pH Distributions .............. 135
IV-9. Stations Monitored by CH2M Hill,June 1972-July 1975 . 138
IV-10. Stations Monitored by CH2M Hill, July 1975-October
1975 139
rv-11. Major STORET Stations: Inner Bellingham Bay 144
IV-12. Major STORET Stations: Northern Bellingham Bay . . . 145
IV-13. Major STORET Stations: Rosario Appendage 146
IV-14a. Time History of SSL at STORET Stations BLL006 and
BLL008 . 147
IV-14b. Time History of SSL at STORET Stations BLL009 and
BLL010 148
V-l. Percent Larval Abnormalities Versus SWL for the
Bellingham-Anacortes and Port Angeles Areas. .... 154
V-2. Maximum Observations of Surface SSL. 168
V-3. Maximum and Minimum Observations of SSL in Bellingham
Harbor ( 169
V-4. Live-box Locations in Bellingham Bay ........ 170
-ix
-------
V-5. Juvenile Salmon Bioassay Stations. 173
V-6. Three Responses of Fertilized English Sole Eggs to
Various Concentrations of SWL. ..... 177
V—7. Locations Sampled in North Puget Sound Historical
Biomonitoring. ............ 181
V-8. Proposed Sequence of Reactions for the Degradation
of Chlorine in Aquatic Systems , . . . . . . . . . . 186
VI-1. Bellingham-Samish Bay Biological Study Area 201
VI-2. Phytoplankton and Zooplankton Sampling Stations. „ . 205
VI-3. The Relationship of Phytoplankton Productivity Rate
per mg of Chlorophyll A vs. SSL Concentration for
Samples Collected at the Surface at Temperatures Equal
to or Greater than 10° 207
VI-4. Average Surface SSL - Data from University of Washing-
ton Study of November 1959-November 1961 209
VI-5. Station Locations at which Flatfish Eggs Were Collected
and Water Quality Determined 212
VI-6. Shellfish Beds near Hale Passage, Sinclair Island
and Guemes Island. 219
VI-7» Diversity Indices of Invertebrates in the Bellingham
Bay Region 223
VI-8. Average Total Number of Invertebrate Species Found
in a Triplicate Sample Taken in 1977 225
VI-9. Sample Station Locations for the CH2M Hill Study on
Abundance and Diversity of Benthos off Post Point. . 228
VI-10. Diversity Index Periodicity of Benthic Invertebrates
off Post Point from 1972-1975. 230
VI—11. Organism Abundance Periodicity off Post Point from
1972-1975 232
VI-12. Areas of Similar Fauna and Diversity 234
VI-13. Sludge Deposits in Whatcom Waterway and Bellingham
Harbor 236
VI-14. Characteristics of Bottom Sediments in Bellingham
Harbor and Contiguous Parts of Bellingham Bay. . . . 237
VI-15. Total Number of Benthos per sample vs. Percent
Volatile Solids in the Sediments of Bellingham Harbor 238
VI-16. Inventory of Salmon Utilization in Bellingham and
Samish Bays 247
VI-17. Chum, Chinook and Coho Concentrated Migration Areas. 256
VI-18. Location of Herring Spawn Observed During Spawning
Ground Surveys in Hale Passage, 1972-1979 263
VI-19. Location of Herring Spawn Observed During Spawning
Ground Surveys in Samish Bay, 1973-1977 267
-x-
-------
Page
VI-20. Harbor Seal Locations in Bellingham and Samish Bays
Observed During Aerial Survey Counts 271
VI-21. Observation Locations of Whales In the Bellingham-
Samish Bay Areas ... . 273
VI-22. Movements of "J" Pod of Killer Whales in Puget Sound
and the Strait of Juan de Fuca, 1976-1977. . . . ; . 276
VI-23. Biologically Significant Areas of Bellingham Bay . . 282
VI-24. Biologically Significant Areas of Samish Bay .... 283
VI-25. Documented Nested Sightings in Bellingham and Samish
Bays 285
VIi-1. Shallow Sublittoral Food Web in Mud/Eelgrass Habitat
Near Bellingham Bay - Spring Food Web. . . 295
VII-2i Shallow Sublittoral Food Web in Mud/Eelgrass Habitat
Near Bellingham Bay - Fall Food Web. . 296
VII-3. Habitat Types in Bellingham Bay 299
VII-4. Species Known to be Detrimentally Affected by Sulfite
or Other Mill Effluents • . . 300
VII-5. Neritic Food Web Near Bellingham Bay with Species
Known to be Detrimentally Affected by Sulfite or
Other Mill Effluents 301
VIII-1. Mean Current Patterns in the Rosario Appendage . . . 310
VIII-2. Average Salinity and SWL Concentrations 313
VIII-3a. Percentage of the Time the Wind Blows from Individual
and Grouped Directions During Each Month 315
VIII-3b. Hourly Vectors from 17 April to 7 May 1963 of Raw
Current Speed and Direction, and Wind Speed and
Direction 316
VIII-3c. Hourly Vectors from 7-28 May 1963 of Raw Current
Speed and Direction, and Wind Speed 317
VIII-3d. Tidally Smoothed Current Meter Records Within
Bellingham Bay Versus Runoff and Wind Conditions . . 318
VIIl-4. Flood Tide Currents in Bellingham Bay. ....... 319
VIII-5. Composite Pattern of Mean Currents 320
VIII-6. Texaco Pier Oil Spill Dispersion Pattern, April 26,
1971 322
VIII--7. Estuarine Classification Diagram of Hansen and
Rattray as Adapted by Conomos 323
VIII-8a. Profile Distribution at Mid-channel from the Pacific
ocean to the Head of Puget Sound of Tidal Kinetic
Energy, Near Bottom Freshwater Percentage and Salinity
and Near Bottom Oxygen Saturation and Concentration. 326
-xi-
-------
Page
VIlI-8b, Profile Distribution of the Measured Variance of
Current Meter Records Taken at Mid-channel in Rosar-
io Strait, Bellingham and Guernes Channels, and into
Bellingham and Padilla Bays 326
YIII-9.' Kinetic Energy Computed From Tides Versus Variance
from Current Meter Measurements. . . . . .. . . . . . 327
Vlil-IQ. Surface Distribution of Temper attire, Salinity, SWL
and Winds for 3-4 November 1960 . . . 330
VTII-11. Surface Distribution of Temperature, Salinity, SWL
and Winds for 21-22 June 1960. ........... 331"
VIli-12. Surface Distribution of Temperature, Salinity, SWL
and Winds for 23-24 August 1960 . 333
V2II-13. Patterns of Surface SWL. ....... 335
VIII-14. Approximate SWL Concentration Near Mid-Bellinghaio
Bay Before, During and After A Georgia-Pacific Labor
Strike 336
VIII-15. Selected Water Quality Stations Sampled by the
Washington Department of Fisheries . 339
VTII-16. Waste Sources in the Anacortes Area. . . 340
VIII-17. SWL and Salinity Versus the Shortest Distance by
Water to the Station from the Georgia-Pacific Mill
and the Nooksack River . ......... 342
Vlli-18. Selected Water Quality Stations Used in this Report. 344
VIII-19a. Time History of Dissolved Oxygen at STORET Stations
BLL0G6 and BLL0G8 . . 350
Vlll-19b. Time History of Dissolved Oxygen at STORET Stations
BLL009 and BLL01Q 351
VIII-20. Comparison of Mean Percent Abnormal Response of
Oyster Larvae at 32 Stations . . 357
VIXI-21. Stations Sampled for PBI and Percent Abnormality . . 372
Vili-22. Effect of Pulp Mill Closure on Water Quality and
Oyster Larvae Response in the Bellingham-Anacortes
Area 373
¦xii-
-------
LIST OF TABLES
Page
1-1. Historical Summary of Georgia-Pacific Pulp and Paper
Mill, Bellingham, Washington .... 7
1-2. History of Known Discharge Points, Georgia-Pacific . . 8
1-3. History of Known Effluent Discharges, Georgia-Pacific. 9
1-4. Waste Flow Limitations Specified in the WPCC Permits
Issued to Georgia-Pacific 19
1-5. Summary of the Compliance Dates in WPCC Permit
No. T-2862 21
1-6. Final Effluent Limitations and Compliance Dates for
Georgia-Pacific NPDES Permits (WA-00109-1) ...... 24•
1-7. Reported Spills and/or Violations, Georgia-Pacific . . 30
II-l. Known Surface Water and Ground Discharge Sources in
the Bellingham Bay Area 40
II-2. Average Annual Discharges of Waste Water to Bellingham
Bay, 1966 - 1979 45
II-3. Summary of Surface Water Industrial Discharge Sources
and Diversions to Sewage Treatment Plants 61
II-4. Summary of Municipal Discharge Sources and Diversions
to Sewage Treatment Plants 62
II-5. Treatment Process Utilized by Municipal and Domestic
Facilities Discharging to Bellingham Bay ....... 67
II-6. Summary of Documented Mill Closures at Georgia-Pacific,
1964 - 1979 72
II-7. Known and Suspected Toxic Compounds in Mill Effluent
for Bleached Sulfite Pulpmills ..... 76
II-8. Constituents present in the Effluent Waters of Georgia-
Pacific's Pulpmill and Chlor/Alkali Plant. 77
II-9. Concentrations of Effluent Constituents Discharged by
Georgia-Pacific 78
11-10. Concentrations of other Pacific Northwest Pulp and
Paper Mill Constituents, Sulfite Mills . 79
III-l. Sill Depths within the Study Area 88
III-2. Characteristic Dimensions and Ratios of Rosario
Appendage 90
IV-1. Water Quality Criteria for Class A and B Marine Waters 117
IV-2. Bellingham Bay Sampling Study Summary . .120
IV-3. Summary of Surface Water Quality Parameters for CH2M
Hill Data 140
IV-4. Summary of Surface Water Quality Parameters for
-xiii-
-------
Paae
V-l. Acute Effects of SME & SSL on Aquatic Life 155
V-2. Sublethal Effects of Sulfite Mill Effluents on
Aquatic Life .............. 157
V-3. Georgia-Pacific Bioassay Results 161
V-4. Maximum Tolerance Limits of SSL for 190 Day Old Salmon. 165
V-5. Maximum Tolerance Limits of SSL for 2 Age Groups
of Chinook Salmon. . . . 165
V-6. Apparent Tolerance Levels for Salmon . ... 166
V-7. Summary of Data Pertaining to Bellingham Bay Pollution
Study. . . . . 171
V-8. Percent Mortalities at Termination of Tests and Summary
of Water Quality Data 174
V-9. Increase in Response of English Sole Eggs to Increasing
Concentrations of SWL. 178
V-10. Comparison of WDF Compendium Data 180
V-ll. Major Compounds Identified in Sulfite Pulping Opera-
tions. 183
V-12. Toxicity of Chlorine to Marine Organisms in Puget Sound
and Adjacent Waters
VI-1. Major Organic Groups Occurring in Bellingham Bay . . .200
VI-2. Major and Minor Phytoplankton Genera of Bellingham Bay 203
VI-3. Summary of Phytoplankton Productivity Rate per Unit
of Chlorphyll A. .... 208
VI-4. Flatfish Egg Distribution in the Bellingham Area . . . 213
VI-5. Faunal List of the Bellingham Zooplankton 216
VI-6a. Mean Values of Properties Measured at the Surface in
Bellingham Area; Plankton Study. ........... 217
VI-6b. Mean Values of Properties Measured at 20 Feet in the
Bellingham Area; Plankton Study . 217
VI-7. Shellfish Beds in the Bellingham Bay Region 220
VI-8. Crab Landings in Bellingham-Samish Area. . 226
VI-9. CH2M Hill Data for Eight Locations off Post Point. . . 229
VI-10. CH2M Hill Data for Eight Locations off Post Point. . . 231
VI-11. Fishery Studies Conducted in Bellingham 6 Samish Bays. 241
VI-12. Standard Herring Spawning Intensities. . . 245
VI-13. Freshwater Life Cycle of Salmon and Anadromous Trout
Species in Freshwater Tributaries Flowing to Belling-
ham Bay 248
VI-14. Freshwater Life Cycle of Salmon and Anadromous Trout
Species in Freshwater Tributaries Flowing to Samish
Bay • 249
-xiv-
-------
Page
VI-15. Marine Species Occurring in Bellingham Bay . . ... . 258
VI-16. Dominant Marine Pish in Bellingham Bay 261
VI-17. Summary of Spawning Activities in Hale Pass 262
VI-18. Marine Mammal Species Common to Northern Puget Sound . 269
VI-19. Aerial Survey Counts of Harbor Seals in Bellingham
and Scunish Bays 272
VI-20. Observations of Cetaceans in the Bellingham-Samish
Bay Area 274
VI-21. Available Geographical Bird Habitats in Bellingham
and Samish Bays 279
VI-22. Key to Figures VI-23 and VI-24 281
Vl-23. Biologically Significant Areas in Bellingham and Samish
Bays, Birds 284
VII-1. Minimum of Known Marine Genera at Port Townsend, Port
Angeles, and Bellingham Bay, Washington 293
VII-2. Degree of Overlap of Species Groups Between Bellingham
Bay and Nearby Areas with Know Trophic Structures. . . 297
VIII-1. Seasonal Water Quality Measurements and Violations in
Inner Bellingham Bay . 346
VIII-2. Surface DO Levels at Comparable Stations Before and
After Installation of Primary Treatment. . . 348
VIII-3. Summary of WDF Compendium Data for Years and Depths
Prior to and Following Primary Effluent Treatment. . . 355
VIII-4. Historical Variation in Quality and Acute Toxicity to
Pacific Oyster Larvae of Surface Receiving Water ... 359
VIII-5. Effect of Various Factors on Abnormal Shell Development
and Mortality of Pacific Oyster Larvae in Bellingham
Bay Surface Water Samples 362
VIII-6. Significant Annual Variation in Abnormality and
Mortality of Pacific Oyster Larvae .... 363
Vlll-7 . Variation in Receiving Water Quality and Toxicity to
Oyster Larvae . 364
VIII-8. Variation in Abnormal Shell Development of Oyster
Larvae as a Function of Season, Location and Depth
of Sampling as well as PBI, Salinity and the Age of
Seawater . 366
VIII-9. Variation in Mortality of Oyster Larvae as a Function
of Season, Location and Depth of Sampling as well as
PBI, Salinity and the Age of Seawater 367
VIII-10. Significance of the Variation in Abnormality and
Mortality of Pacific Oyster Larvae ,369
VIII-11. Effect of Pulpmill Closure on Water Quality and Oyster
Larvae Response in the Bellingham-Anacortes Area ... 371
-xv-
-------
EXECUTIVE SUMMARY
The Georgia-Pacific pulp and paper mill (originally Puget Sound
Pulp and Timber) has discharged sulfite and other waste into
Whatcom Waterway and Northern Bellingham Bay for more than 50
years. The mill is multi-faceted in its processes and opera-
tions . In addition to the main sulfite operation, pulping
processes include extensive by-product recovery, a semi-
chemical groundwood process, and a chlor/alkali plant which
generates chlorine and caustic soda. The mill installed secon-
dary treatment 11 months after the date required by federal
permits and regulations. During this time it discharged primary
waste to the nearshore zone at the northwest corner of the bay.
Following the installation of secondary treatment in June 1979,
the mill now discharges from a secondary treatment lagoon via a
submarine diffuser into the open waters of the bay.
Oceanographic analysis of tides and currents revealed a southward
flow from the Bay at all depths, although surface flows showed wind
induced fluctuations. Waters exit the Bellingham - Samish Bay
system primarily between Vendovi and Samish Islands re-entering
Rosario Strait through Bellingham and Guemes Channels. Cur-
rent fluctuations in the Bay (which indicate the kinetic energy)
are tenfold less than Rosario Strait, but greatly exceed computed
values for the Bay based on tidal energy alone. The excess energy
is hypothesized to result from wind effects and dynamic estuarine
processes from Nooksack River flow.
Bay water in the Bellingham system is thought to originate pri-
marily from mid-depth water in the Strait of Georgia. The
residence time of water in the Bellingham system can vary between
1 and 11 days; however, existing data indicate a typical residence
time of'4 -5 days. Water or effluents exiting the Bellingham -
Samish system enter Rosario Strait and may then be transported
over a wide area of the Inner Strait of Juan de Fuca.
Dilution of Georgia-Pacific effluent is generally slow even
though initial dilution (1:121) is similar to that found at
-1-
-------
West Point in Seattle and at Port Angeles (Evans-Hamilton, Inc.,
unpublished dataJ. A total dilution of 35,QQQ to 1 is reached
at approximately 15 -20 km. By comparison, effluent from the
Scott Paper Mill, previously operating at Anacortes, reached a
dilution of 37,000:1 within 2.5 km of the outfall. ' Georgia-
Pacific emits 5-6 times the effluent from the second largest
source (B&llingham STPJ and over 30 times that of the third
largest source in the Bay.
Water quality violations caused by primary treated effluent in-
clude violations of DO and BOO. The mill exceeded permitted
daily average limitations on BOD discharge during most of the 11
months prior to compliance with secondary treatment. DO violations
resulting from primary mill effluent have been observed in various
locations in northern Bellingham Bay; however, violations have been
most severe in the area of the I and J waterways and Whatcom
Waterway adjacent to the pulpmill discharges. Long term water
quality shows a decreasing trend in spent sulfite liquor (SSL)
discharges and a slow improvement in DO values between the I960's
and late 1970's as various treatment improvements have been made.
Low pH value was recorded adj acent to the mill prior to primary
treatment; however, this improved considerably in recent years.
Mill effluent has been shown to be highly toxic in early bioassays
conducted by Georgia-Pacific. More recent bioassays show technical
compliance with permit requirements; however, the methodology
and computations of LC50 levels remain in some doubt.
Studies of the toxic nature of Georgia-Pacific effluents have been
performed by state and federal agencies using fish, fish eggs
and oysters as test organisms. Tests with eggs, juvenile and
mature fish have.all shown acute effects of sulfite mill effluents.
Threshold levels measuring as low as 14 ppm SSL seem to have
measurable effects on survival, particularly in younger organisms.
Tests on oyster larvae have shown a somewhat periodic pattern of
-2-
-------
toxicity based on limited monitoring. Effects on both survival
(mortality) and development (abnormality) have been shown for
these indicator organisms. Studies have shown both a decrease in
toxic effects with increasing distance from the mill and a de-
crease with time following a two-week shutdown in mill production.
Effluents from the sulfite mill have been shown to traverse areas
of high biological habitat value. Strong evidence exists that
the effluents limit biological productivity and diversity,
particularly in the inner harbor. The typical effluent paths
traverse areas in which eelgrass, commercial and recreational
fish and shellfish, marine birds and marine mammals utilize the
bay waters for habitat. A host of smaller organisms which
support these species also show effects from the effluent. Bio-
logical literature and data from sulfite mill effluent supports
the conclusion that numerous types (species) of organisms are
affected by sulfite effluent and that secondary treatment
often reduces the toxicity. Toxic components of sulfite
effluent have been identified, although bioassay studies are
typically conducted with whole effluent. An analysis of potential
chronic or sublethal effects acting through the ecological food
web have been shown to be a logical effect based on toxicological
literature and the present state of knowledge of Bellingham Bay
area ecosystems.
-3-
-------
I. HISTORY OF THE GEORGIA-PACIFIC PULP AND PAPER MILL AT
BELLINGHAM, WASHINGTON
The Georgia-Pacific Corporation, Puget Sound Division, operates
a pulp and paper mill facility in Bellingham, Washington. The
facilities were originally the Puget Sound Pulp and Timber
Company, which began pulping operations in Bellinghaxn during 1928
or earlier (Application No. Q71-OYB-2-OOOOS1). The pulpmill was
established at the entrance to Whatcom Waterway (Figure 1-1),
along a railroad line of the Burlington Northern Company, so as
to have both land and sea access for raw materials and shipment
of products.
During World War II, the federal government, in an effort to
increase needed alcohol production, set up a pilot plant, with
Puget Sound Pulp and Timber as leasee to produce alcohol. The
plant was purchased from the government by Puget Sound Pulp and|
Timber in 1947, resulting in the integration of the plant into
the overall mill processes (Bellinghaxn Herald, February 11, 1970).
Over the next two decades, Puget Sound Pulp and Timber conducted
research efforts aimed at expanding the principle of by-product
recovery. By the 1960's they produced:
» ethyl alcohol
• ingredients in animal foods
• adhesives
• components of pharmaceuticals and building compounds
• tanning chemicals
• numerous other compounds
The recovery of over 50 chemical compounds from process wastes
made Georgia-Pacific unique among Puget Sound mills in its
methods of operation (PCHB Stipulation No. 867, November 23,
1976).
-4-
-------
0 1000 2000
Luramt
Indian*
Reservation
Bellingham
Bay
Post
Point
Chuekanut
Bay
PlMunt
Governors B«y
Point
Figure 1-1 LOCATION OF THE GEORGIA-PACIFIC PULP AND PAPER MILL
IN RELATION TO NORTHERN BELLINGHAM BAY.
-5-
-------
Puget Sound Pulp and Timber Company was acquired by Georgia-
Pacific Corporation in 1963, when it became the Puget Sound
Division of Georgia-Pacific (Bellingham Herald, February 11,
1970). Since that time, the mill has gone through various
modifications of processes and effluent treatment. The history
of these modifications has been derived from permits, permit
applications and fact sheets, and general correspondence on
file at the Washington Department of Ecology (DOE), Olympia,
Washington; and the U.S. Environmental Protection Agency (EPA),
Region X, Seattle, Washington. This correspondence is incomplete
during certain time periods, yielding an historical sketch with
minor data gaps. Little historical data exists prior to the
late 1960's. Summary tables of pulping processes, treatment
installations, discharge points and effluents are presented in
Tables 1-1, 1-2, and 1-3.
The history of the Georgia-Pacific Pulp and Paper Mill is
described in detail in the four sections of this chapter with
respect to:
• Processes and Operations (including treatment pro-
cesses)
• Permits and Regulations
• Compliance History
• Spills and Violations
These sections supply the necessary background for Chapters II-
VII, which deal with physical and biological aspects of aquatic
systems in Bellingham Bay and adjacent waters.
A. PROCESSES AND OPERATIONS
1. Initial Operations
The Georgia-Pacific Corporation Pulp and Paper Mill complex is
located in the northeast corner of Bellingham Bay adjacent to
the Bellingham Central Business District (Figure 1-2).
-6-
-------
Table 1-1. HISTORICAL SUMMARY OF GEORGIA-PACIFIC PULP AND
PAPER MILL, BELLINGHAM, WASHINGTON.
Began Operation; 1928
Initial Process: Calcium based sulfite, semi-chemical groundwood.
Process Cnanges or Modifications;
1943 Alcohol recovery plant installed.
1965 Began operation of chlor/alkali plant.
1971 Increased by-product recovery, lignin processing,
and evaporation capacity.
7/70 Installed mercury recovery system (chlor/alkali
plant).
12/73 Installed mercury sulfide process (chlor/alkali
plant).
5/79 Submarine diffuser operational.
Primary Treatment:
Required by: September 30, 1970.
Operational by: April 197 3.
Treatment: Clarifier.
Secondary Treatment:
Required by: July 1, 1978 (State of Washington changed
date to September 30, 1978).
Operational by: June 7, 1979.
Treatment: Aerated stabilization basin.
-7-
-------
Table, 1-2. HISTORY OF KNOWN DISCHARGE POINTS, GEORGIA-PACIFIC
PULP AND PAPER MILL, BELLINGHAM, WASHINGTON.
Date
1928 - 1938
1938 - 1945
1945 - 1946
1946 - 1947
1947 - 1965
1965 - 4/73
4/73 - 6/79
6/79 - present
Discharge Points in Operation
6
6, 4
3, 4, 6
2, 3, 4, 6
1, 2, 3, 4, 5, 6, 8
1, 2, 3, 4, 5, 6, 7, 8
3, 5, 7, 8
9 (combined 3, 5, 7, &,8)
8
-------
Table 1-3. HISTORY OF KNOWN EFFLUENT DISCHARGES, GEORGIA-PACIFIC PULP AND PAPER MILL, BELLINGHAM, WASHINGTON
Average Waste
Known Amounts
Dates Outfall No. Type (mgd average)
1928 - 1938 6 Calcium base sulfite pulping waste . N/D
1938 - 1945 6, 4 Calcium base sulfite pulping waste; Alcohol plant wastes N/D
i
1945 - 1946 3, 4, 6 Calcium base sulfite pulping waste; Alcohol plant wastes N/D
1946 - 1947
1947 - 1965
1965 - 4/73
4/73 - 6/79
2, 3, 4, 6 Calcium base sulfite pulping waste; Alcohol plant wastes
1, 2, 3, 4, Calcium base sulfite pulping waste; Semi-chemical pulping waste;
5, 6, 8 Paper-grade pulping wastes; Alcohol plant waste
1, 2, 3, 4, Calcium base sulfite pulping waste;
5, 6, 7, 8 Semi-chemical pulping wastes;
Paper-grade pulping wastes;
Alcohol, chlor/alkali, sulfuric acid and other by-product wastes
3, 5, 7, 8 Primary Treated Process waste from:
Calcium base sulfite pulping
Semi-chemical pulping
Paper-grade pulping
Alcohol, sulfuric acid plants and other by-products
Treated waste from chlor/alkali plant
N/D
N/D
1965-1966: 57.9*
1966-1967: 36.29
1967-1973: 41.66*
1974-1975: 45.23*
1976-1979: 47.20*
6/79 - 9 Secondary Treated Process waste from: N/D
present Calcium base sulfite pulping
Semi-chemical pulping
Paper-grade pulping
Alcohol and sulfuric acid plants and other by-products
Treated waste, from chlor/alkali plant
* Maximum waste flows
** N/D available for chlorine plant
-------
.V.V.'.'.V/.V.ViVAV/.V.V.'.V
Bellingham
Bay
/
/
.v.y.v.y.vj
//
Vv:;x£X;X:'>;*^
t- ¦*¦'•*•*.*•**'*I;Xv;;X;'vXvX;X;X;yX;X;
XvtvI*Xf.vX\*X
vv!v
.... J::::::::::::::;::
?X*I* <^X'X*X*X* •X\*X*X'X*XvX,X*X,,Xv
-v.v.v.vjw.'.'.'.'.v.v.v.'w.'.'.v.'.'.v, ...
vxvx-xxx+xx-x-x-x'xw
x£x£:::::^
/ '
V'.V.*.\\*.V. ••.~.V.V.V.Vv.v-v.w.v.v.vv«v.*.»
_ - /,,,*,',V.'.V.V,V.,.,.,.,.*.V,T.V.*.V.V.,.*.,.V.V.VAV.V
IT-: xx-x-x-x-xx-x:x-x^:'x-:^xvx0x-x%v:vx\-x-x-x-xvxvx-x-x-:
/
/
tvX,>X^>>X»VW*X"X*'.vX*X,XfcXv>>X<*Xr
kX#;X:X;^^^
"//.vlvlvlvlv.'.'.v.'.'.v,
¦•¦.••v.
.V.V.V.V.'.V.V
1*1*1*1*1*1*1*1*1
WAV.'•'V.V.V
X*X*XvX,X*>X*
200 400
100 300 500
,v.
>X*X"XvX*XvX*
Figure 1-2
OUTFALLS OF GEORGIA-PACIFIC PULP AND
RELATION TO THE BELLINGHAM BAY INNER
PAPER MILL IN
HARBOR AREA
—10—
-------
The mill'produces paper products (both high grade paper and
tissue paper) and uses three varieties of pulping processes? sul-
fite , semi -chemical groundwood and paper grades. The sulfite
process, which produces.the majority of mill effluent, uses
calcium as a base. The semi-chemical pulping process is.currently
identified by Georgia-Pacific as the "Permachem" process which
uses a base of sodium sulfite. Both processes use an acidic
sulfite liquor to break down wood fiber derived from chips into
components usable, in the paper making.processw Additional infor-
mation on sulfite and semi-chemical pulping processes is explained
in Britt (1970) and other reference sources.
The paper grade pulp is derived from waste paper (newspapers).
The wastepaper is de-inked and mechanically pulped by beaters .
The resulting pulp is used to produce paperboard and packaging-,
material. The mill produces roughly one sixth of the total putfp
volume via the semi-chemical process, with the majority through
calcium based sulfite (DOE Fact Sheet, March 19, 1972). The overall
operational plan of the mill is shown in Figure 1-3.
In addition to the basic pulp and paper making processes, Georgia-
Pacific has a separate chlor/alkali plant which uses salt to
generate chlorine and caustic soda (sodium hypochlorite, sodium
chlorate). The mill also has a large number of by-product re-
covery processes which include an alcohol recovery plant, lignin
products recovery system, sulfuric acid recovery plant, and
numerous other minor recovery and by-product systems.
During its early history, the Georgia-Pacific mill had between
six and eight dischargers which fed into Whatcom Waterway
directly or through the log holding pond via nearshore outfalls.
The 1962 permit application (Permit No. 1861) shows five dis-
charge sewers; #1 discharged via the log pond and #2-5 discharged
along the edge of the Whatcom Waterway. The tissue paper plant
also discharged to Whatcom Waterway, apparently via Outfall #6
(Permit No. 1979, October 1, 1963). The chlor/alkali plant
-11-
-------
Figure 1-3 "SCHEMATIC OF HATER FLOW" FOR GEORGIA-PACIFIC CORP., BELLINGHAM, WASHINGTON
Source: Application Submitted July 28, 1978
Clear
#3 sewer
Clari-
fier
~-Net steam
MGPD
#5 sewer
Municipal Sanitary
Sewer
H2SOi(
To
Secondary
Treatment
Lagoon
Alcohol
Clean
Clear
To Secondary
Bleach
Plant
Acid Plant-
Pulp Cooking
Liquor &
H2S0U
Bleached
Sulfite Pulp
Machine
Room
Filter
Plant
Alcohol
Liquor
Recovery
& Screen
Room
Steam
Plant
Chlor/
Alkali
Plant
LigniA
By-
products
Permachem
Tissue
Products
Hydraulic
Barking
Plant
Paperboard
Digester
and
Blow
System
Treatment Lagoon
-------
discharged through Outfall #7 beginning in October .1964, or
possibly earlier (Permit No. 2094, October 19, 1964). Beginning
in late 1947, available correspondence indicates effluent (cool-
ing water and wastewater) from the alcohol plant was discharged
to Bellingham Bay via the Municipal storm sewer line (Outfall #8)'
until April 1973 (Application No. 071-OYB-2-000081).
The mill continued to discharge in basically the same configur-
ation (eight outfalls) until the installation of primary treatment
(which preceeded filling of the log pond) in 1973, at which point
Outfalls #1,2, 4 and 6 were rerouted and combined with the
clarifier, which then discharged through Outfall #5. The 1973
application shows Outfalls #3, 5 and 8 discharging from the main
mill. Outfalls #1 (paperboard mill), #2 (barking and chipping
plant), #4 (blowpits), and #6 (tissue mill, etc.) were combined
with untreated bleach plant effluent, lignin products effluent
and filter backwash which were also discharged through Outfall #5.
Subsequent to primary treatment installation, Outfall #8 was
to discharge only cooling water to Whatcom Waterway in the
nearshore area (Johnson, personal communication, Jan. 16, 1980).
In 1979, Sewers #3, 5 and 8 were combined, with the initiation of
secondary treatment. Their effluent is currently pumped to deeper
waters of Bellingham Bay through the submarine diffuser (labeled
Outfall # 9). The chlor/alkali plant (Outfall #7) was also
combined with Outfall # 9 in 1979, although the treated caustic
effluent from the plant is received in a separate compartment
of the secondary treatment lagoon previous to discharge (Johnson,
personal communication, 1980).
-13-
-------
2. Primary Treatment
According to Georgia-Pacific Permit No. T-2862, primary treatment
was originally scheduled for September 30, 1970. In 1969, however.
Georgia-Pacific requested a time extension in order to explore
the possibility of joint primary treatment with the City of
Bellingham. The outcome of 3 report by CH2M Hill engineers was
a decision to use separate systems, for which Georgia-Pacific
submitted revised plans in June 1971 (Dahlgren, letter of
October 5, 1971). Permit objections for the proposed clarifier
site by the Corps of Engineers resulted in further delays while
Georgia-Pacific personnel explored possibilities of treatment
processes which occupied less space (Dahlgren, letter of Decem-
ber 21, 1971).
As the main possibility for ail alternative treatment system,
Georgia-Pacific ordered a pilot model lamellar separator from
the manufacturer in Sweden (Dahlgren, letter of October 5, 1971).
Problems with dock strikes on the east coast, customs and land
shipment resulted in a delay of several months in pilot equip-
ment arrival. The pilot lamellar separator did arrive in January
1971 and was tested briefly, showing that it offered significant
efficiency and reduction of space requirement (Dunkak, letter
of January 26, 1972). By March 3, 1972, however, Georgia-Pacific
decided that insufficient time remained to put the lamellar
separator on line. The mill therefore proceeded with the
installation of a conventional clarifier system (Dunkak, letter
of March 3,1972) with a target date of November 1972. Appar-
ently further delays occurred; however, the reason is not
known because there is a correspondence gap in DOE files
for late 1972. In mid-April 1973, Georgia-Pacific began
primary treatment with only minor startup problems
(Dahlgren, letter of May 1, 1973); however, spills from the
clarifier occurred periodically over the next several years
(Mowry, letter of January 11, 1974, February 28, 1975, April
26, 1977, July 15, 1977, and July 26, 1977; Moore, letter of
August 2, 1976).
-14
-------
3. Secondary Treatment
Georgia-Pacific's 1975 National Pollution Discharge Elimination
System (NPDES) permit required reduction of discharge of BOD,
solids and SSL through installation of secondary treatment or
its equivalent. Federal guidelines specified that final effluent
limitations were to be met by July 1, 1977 (Smith, letter of
April 11, 1975). A tentative compliance schedule for Georgia-Pacific's
permit issued by DOE (DOE, memo of March 17, 1975) showed that
Georgia-Pacific would be required to install waste treatment sys-
tems by the following dates:
January 1, 1977:
• SSL recovery system (conversion to blow tanks,
SSL recovery washers, conversion to rotary, screens,
revise bleaching system and install SO2 stripping
column to prepare SSL for fermentation)
• Permachem Liquor recovery
• Yeast recovery
• Alcohol plant modifications
July 1, 1977:
• Lignin products modification
• Other effluent treatment (hydraulic barking, pulp
drying, etc.)
• Upgrade primary treatment through BOD removal
July 31, 1978:
• Condensate treatment
• Bleach plant recovery (BOD reduction in Bleach plant
effluents)
thus effectively requiring secondary treatment by July 1, 1977,
as required by the Federal Water Pollution Control Act (FWPCA).
In April, however, DOE notified EPA of its intent to use less
stringent effluent regulations and to extend the time requirements
for secondary treatment by one year to July 1, 1978 (Burkhalter,
letter of April 4, 1975). In response to this, EPA indicated that
-15-
-------
while the federal government was willing to accede to the less
stringent effluent requirements, the date required by FWPCA.
(July 1, 1977) must be met (Smith, letter of April 11, 1975).
Further correspondence from DOE urged reconsideration of the
deadline in light of the benefits of the new technology,
"Baierl Process," which Georgia-Pacific proposed to use for
secondary treatment. The process would recover chemicals from
the waste streams which could be used for by-product manufac-
ture (Behlke, letter of April 17, 1975). EPA agreed with the
July 1, 1978 secondary treatment compliance data provided
Georgia-Pacific use the extra time to pursue both the "Baierl
Process" and other treatment possibilities (Smith, letter of
April 29, 1975).
The permit was issued and subsequently appealed to the Pollu-
tion Control Hearings Board in June 1975. Out of the settle-
ment of this appeal (PCHB Stipulation #867) came a reissuance
(November 30, 1976) of the permits (Reissued Permit No. WA-000109-1)
by DOE with the new date for final effluent limitation compli-
ance set at September 30, 1978 (Provost, document of May 13,
1975; Docket No. DE-77-195).
Georgia-Pacific submitted plans for waste recovery treatment
in July 1976, which were approved by DOE (Provost, letter of
July 14, 1976); however, these plans were apparently for the
more complicated secondary treatment systems being proposed
by Georgia-Pacific at that time. Georgia-Pacific then decided
that an aerated stabilization basin was more feasible, and pre-
liminary plans for the secondary treatment lagoon were approved
in March 1977 (Provost, letter of March 9, 1977). Preliminary
plans for the diffuser outfall were approved in May 1977
(Provost, letter of May 10, 1977). Final plans on the lagoon
and diffuser submitted to DOE in June 1977 were judged inade-
quate by DOE (Johnson, letter of July 21, 1977) and approval
16-
-------
was not forthcoming until January 1978 (Burkhalter, letter of
January 23, 1978).
Early in 1978, Georgia-Pacific issued an Environmental Impact
Statement (EIS) on the treatment lagoon and began applying for
federal and state permits. Following several delays due to
objections by state and federal agencies (Hallauer, letter of
March 20, 1978; Blum, letter of May 11, 1978) permits were issued
in April (shorelines permits) and June of 1978 (Corps of Engineers
permit) (Mowry, letters of June 1, 1978 and June 9, 1978).
Construction activities on the secondary treatment facili-
ties beganon June 20, 1978 (Mowry, letter of August 7, 1978).
Throughout the construction process, Georgia-Pacific claimed prob-
lems with weather, parts, contractors and equipment malfunc-
tions, all of which apparently delayed the completion date.
In May 1979, final dye tests were run on the diffuser outfall,
and Georgia-Pacific began testing the lagoon that month.
Georgia-Pacific claimed final compliance on June 7, 1979
(Provost, letter of July 31, 1979).
Following start-up of secondary treatment facilities in June
1979, the lagoon dike began to leak and discharge partially
treated effluent to Whatcom Waterway and the Bay (Stanley,
letter of August 3, 1979). This was apparently due to improper
sealing, or construction. The dike continued to leak through-
out the period of most recent available correspondence (Mowry,
letter of September 28, 1979).
B. PERMITS AND REGULATIONS
In 1945 the Washington Pollution Control Commission (WPCC) was
established with the initial task to develop specific
water quality standards (October 8, 1945), By 1955, the
State of Washington initiated a permits program which allowed
-17-
-------
the WPCC to require effluent standards for industries. Seven
WPCC discharge permits issued to Georgia-Pacific in Bellingham
are on file at the Department of Ecology (DOE). These permits
were issued between the years 19S2 and 1973. Originally, the
permits were issued to each of the Georgia-Pacific divisions.
These divisions included sulfite pulping, semi-chemical,
groundwood, tissue products, chlorine and chemical production,
and paperboard. Later, in 1968, the WPCC permits were
issued to Georgia-Pacific Corporation as a whole. Table 1-4
is a list of the issuance and expiration dates for each WPCC
permit and the pertinent division.
1. Pulp and Paper Mill
In general, the WPCC required Georgia-Pacific to submit a
monthly report of the following effluent characteristics
based upon the analysis of daily composited effluent samples:
• Pulp and paper production in tons
• Waste flow (total volume of cooling and con-
taminated water) in gallons
• SCS losses in pounds
• TS losses in pounds
• BOD of discharged waste
In addition, programs and procedures were to be implemented
for the following parameters:
• In-Plant slime control
• Effluent discharge through a submerged outfall
facility
• Treatment of sanitary wastes
• Dredging of sludge beds
• Chipboard unloading improvement
• Primary and secondary treatment facilities
• Foam control
The only effluent characteristic that was consistently placed
under restriction was waste flow. Table 1-4 lists the maximum
waste flow in gallons/day stated in each of the WPCC permits
issued to Georgia-Pacific. The maximum waste flow limit required
18
-------
Table 1-4 WASTE FLOW LIMITATIONS SPECIFIED IN THE WPCC PERMITS ISSUED TO GEORGIA-PACIFIC
Georgia-Pacific
Divisions
Waste flow *
(gallons/day)
Date of Permit
issuance-expiration
WPCC
Permit No.
Sulfite pulping
Semi-Chemical groundwood
Tissue products.
Chlorine plant and chemical
by-products
Paperboard mill
Pulp and paper mill excluding
the chlorine plant
45,000,000
400,000
5,500,000
5,300,000
1,700,000
51,400,000
Dec 18, 1962-Dec 18, 1967
Oct' 1, 1963-Oct 1, 1968
Oct 1, 1963-Oct 1, 1968
Oct 19, 1964-Oct 19, 1969
July 15, 1965-July 15, 1967
May 27 , 1968 - May 15, 1973
1861
1979
1980
2094
T-499
T-2862
*
Note: gallons X 3.785 = liters
-------
for the entire mill in 1968 (51,400,000 gallons/day (194,5ff5,000
liters/day)) coincides closely with the total waste flow permitted
for all of the divisions in the earlier permits, excluding the
chlorine plant (52,400,000 gallons/day (198,334,000 liters/day)).
As a result of the Puget Sound Enforcement Conference, the
WPCC on December 4, 1967 adopted specific water quality stan-
dards for Washington waters and a plan to enact and enforce
these standards. Georgia-Pacific's facilities and effluent
discharge did not meet the new requirements; however, the mill
was allowed to continue discharging as long as corrective
action was taken within a reasonable amount of time (WPCC
Permit No. T-2862).As a result the temporary permit (Permit
No.T-2862)issued to Georgia-Pacific only required a suggested
timetable for compliance.
Temporary Permit T-2862, issued to the Georgia-Pacific Corpora-
tion on May 27, 1968, was the first permit to require the install
lation of primary and secondary treatment facilities. Table 1-5
summarizes the suggested compliance dates placed upon Georgia-
Pacific for primary and secondary treatment, outfall facility
procedures, dredging, and chip barge unloading improvement.
In 1975, the first National Pollution Discharge Elimination
System (NPDES) waste discharge permit was issued to Georgia-
Pacific. Separate permits were issued to the sulfite pu^Pr
paper and chemical complex and the chlor/alkali plant.
Separate permits were not issued to each Georgia-Pacific
division as they were for the WPCC permits. The NPDES per-
mits were far more detailed than the WPCC permits. They
placed limitations and monitoring requirements on such para-
meters as BOD, TSS, pH, temperature and waste flow. Also
included were compliance schedules for:
-20-
-------
Table 1-5 , SUMMARY OF THE COMPLIANCE DATES FOR THE FOLLOWING
' CONDITIONS IN WPCC PERMIT NO. T-2862
Source: Bruce Johnson, letter of Jan. 12, 1972
Condition
Permit
Date
I.A. PRIMARY TREATMENT
1. Preliminary Engineer
2. Final Plans and Specifications
3. Operational
3/31/69
12/31/69
9/30/70
I.B. 80% SSL REDUCTION (to 1800 tons/day)
1. Preliminary Engineer 9/30/70
2. Final 9/30/71
3. Operational 5/15/73
I.C. OUTFALL FACILITY
Feasibility Study & Preliminary Engin- (11/15/73)
eer by 6 months after I.A. & I.B.
I.D. DREDGING
Schedule
Completion by 6 months after I.A.
& I.C.
12/31/69
( 5/15/74)
I.E. CHIPBARGE UNLOADING IMPROVEMENT
Plans
Completion
12/31/69
9/30/70
II.C. SLIME CONTROL REPORT
(No Date)
-21
-------
Primary and secondary treatment
An improved outfall diffuser system
Spill containment and prevention plans
• Solid waste disposal
• Slime control reporting
• Disposal of sanitary sewage
• Oil and hazardous substance liability
• Foam control
• Chip spillage
DOE has record of three NPDES permits issued.to Georgia-Pacific
sulfite pulp, paper and chemical complex. Below are the issuance
and expiration dates for each:
Permit No.
WA-000109-1
WA-000109-1
WA-000109-1
Date issuance-
expiration
May 13, 1975 -
June 30, 1979
May 13, 1975 -
June 30, 1981
June 1, 1979 -
March 31,. 1981
Comments
First NPDES permit
issued on file at DOE
Reissued in accordance
with Pollution Control
Hearing Board No. 867,
effective Nov. 30, 1976
(Biggs, letter of Dec 3, 1976).
Superceded permit No. WA-
000109-1 issued May 13,1975.
The first.permit (May 13, 1975 - June 30, 1979) was issued and
subsequently appealed to the Pollution Control Hearing Board
(PCHB) in June 1975. Out of the settlement of this appeal
(PCHB Stipulation #867) came a re-issuance (November 30, 1976)
of the permit (Reissued Permit No. 000109-1) by DOE with new
effluent limitations and compliance dates (Table 1-6) (Biggs,
letter of December 3, 1976). EPA later vetoed (December 23,
1976) the reissued Permit No. 0000109-1 (PCHB 867 affidavit).
Georgia Pacific was then ordered to comply with its original
NPDES permit (May 13, 1975) and achieve "best practical control
technology as expeditiously as possible" (Order C77-292M
October 5V 1977). A subsequent compliance schedule ordered
by the U.S. Department of Justice required Georgia-Pacific to
-22-
-------
install secondary treatment facilities by May 15, 1979 (Compliance
Schedule No. C77-292M) and later extended this by an additional
30 days (June 15, 1979), but did not waive possible penalties for
non-compliance with the original schedule.
The orginal NPDES permit (No. WA-000109-1) issued May 13, 1975
is recognized by. EPA as the only active permit for the period
from May 13, 1975 to June 1, 1979. For this permit, three
separate interim effluent limitation dates were required as
decribed below.
Daily Average
Interim Period Parameter Limitations
lbs/day (kg/day)
May 13, 1975 - Dec. 31, 1976 BOD 160,000 (73,000)
SCS 27,000 (12,000)
Jan. 1, 1976 - June 30, 1977 BOD 110,000 (50,000,)
SCS 27,000 (12,000=)
A
July 1, 1977 - June 30, 1978 BOD 100,000 (45,000)
SCS 27,000 (12,000)
Final limitations required an average five day BOD of 22,500
lbs/day (10,200 kg/day) and a 35,300 lbs/day (16,000 kg/day)
TSS daily average (Table 1-6).
Additional requirements included:
• Design, construct and operate an improved outfall
diffuser. Construction to be complete by June 30,
1978.
• Develop a toxicity program to be conducted every
six months beginning September 1, 1975. Submittal
of final report to DOE on December 31, 1978.
• Prepare and submit a'Spill Prevention, Containments,
and Countermeasure Plan to DOE by June 30, 1975.
• Beginning July 1, 1978, cease to cause any increase
in water temperature exceeding 61°F in area designated
by DOE.
• Submit a Solid Waste Disposal Plan by December 31,
1975.
• Report annually the in-plant cooling water slime con-
trol program and procedures.
-23-
-------
Table 1-6 FINAL EFFLUENT LIMITATIONS AND COMPLIANCE DATES FOR GEORGIA-PACIFIC NPDES
PERMITS (WA-QOO109-1)
Permit Date
issuance-
expiration
5 day BOD
(lbs/day)*
TSS
(lbs/day)*
Final
Compliance
Period
Daily Ave.
Daily Max.
Daily Ave.
Daily Max.
May 13, 1975-
June 30, 1979
31,000
46,000
27,000
54,000
June 30, 1978-
June 30, 1979
May 13, 1975-
June 30, 1981**
49,000
74,000
40,000
70,000
Sept 30, 1978
June 30, 1981
June 1, 1979-
March 31, 1981
22,500
41,900
35,300
66,100
June 1, 1979-
March 31, 1981
I
to
*1* * Note: pounds X .4536 = kilograms
** Not recognized by EPA.
-------
• Discharge all sanitary sewage to the City of Bellingham
treatment facilities.
• Eliminate visible foam discharge to receiving waters.
• Prevent spillage of wood chips during unloading,
conveying and storing.
Georgia-Pacific is presently operating in accordance with Permit
No. WA-000109-1 (June 1, 1979 - March 31, 1981) which pertains
to both the sulfite pulp, paper and chemical complex and the
chlor/alkali plant. The daily average 5 day BOD and TSS
limitations in lbs/day are 22,500 (10, 200kg/day) and 35,300
(16, 000kg/day) respectively for outfall No. 9 (Figure 1-2)
(Table 1-6). These effluents require daily monitoring. Efflu-
ent pH may not be less than 5.0 or greater than 9.0 and discharges
are not allowed to cause a temperature increase of 0.5°F (0.28°C)
outside of the dilution zone described in the permit. Temper-
ature and pH are to be monitored continuously. A waste flow
limitation was not specified.
Significant provisions of the NPDES permit required the mill
to:
• Submit to DOE an updated Spill Prevention, Contain-
ment, and Countermeasure Plan by September 30, 1979.
• Comply with the solid waste control plan approved by
DOE on June 14, 1977.
• Report annually the in-plant cooling water slime
control program and procedures.
• Discharge all sanitary sewage to the City of Belling-
ham treatment facilities.
• Eliminate visible foam discharge to receiving waters.
• Prevent spillage of wood chips during unloading,
conveying and storing.
• Submit by January 15, 1980 detailed toxicity monitor-
ing results at various effluent concentrations.
2. Chlor/Alkali Plant
Three state and two federal (NPDES) permits were also issued to
Georgia-Pacific's chlor/alkali plant. Below are the issuance
and expiration dates of each permit:
-25-
-------
Permit Number
Date Issued
Date Expired
2094
3456
T-3456
WA-003039-2
WA-000109-1
Oct. 19, 1964
Oct. 16, 1970
Mar. 16, 1973
Feb. 16, 1977
June 1, 1979
Oct. 19, 1969
Oct. 16, 1975
Dec. 31, 1975
June 30, 1981
Mar. 31, 1981
The earliest available permit (No. 2094) indicates a required
maximum wasteflow of 5.3 mgd (20.1 mid). Daily values £or
chlorine, pH and flow were to be submitted to DOE monthly.
Chlorine in the plant effluent was not to exceed 5.0 ppm.
Additional requirements included:
• All plant effluents to be combined in a single
submerged outfall.
• Chemical sludges to be discharged on land and
not allowed to enter State waters.
The subsequent permit (No. 3456) contained additional limita-
tions . These included:
• Submittal of Daily Monitoring Reports of pH, chlorine,
temperature , and mercury to DOE.
• Maximum waste flow of 7.5 mgd (28.4 mid).
• Maximum chlorine residual of 5.0 ppm.
• pH range of 6.5 to 8.5.
• Maximum allowable mercury discharge not to exceed
0.5 lbs/day (.23 kg/day); At no time shall mercury
in effluent exceed .05 mg/1.
• Chemical sludge to be discharged on land and clear
of State water ways.
• Total concentration of mercury in a product pro-
duced by Georgia-Pacific not to exceed 0.25 ppm.
m- Provision of a surge basin to collect contaminated
wastes during emergencies.
After June 30, 1977 the following final effluent limitations
and monitoring requirements were in effect for Outfall # 7.
Total mercury was to be monitored daily and was limited to a
daily average of 0.07 lbs/day (0.032 kg/day). Residual chlorine
26-
-------
could not exceed 5 mg/1 for any 30 minute period and required
continuous monitoring. Effluent pH could not be less than 6.0
or greater than 9.0. TSS was limited to 166 lbs/day (75.3 kg/
day) as a daily average, and was to be monitored daily. Finally,
all mercury contaminated solid wastes were to be disposed of
in a manner that prevented mercury concentrations in excess of
0.025 mg/1 from entering state ground or surface waters.
A major revision in the present permit (WA-000109-1) was the
change in the outfall location for the chlor/alkali plant.
Mercury was the only parameter which had restrictions placed
on it. The daily average could not exceed 0.07 lbs/day (0.032
kg/day). Monitoring of residual chlorine, pH, and TSS was
not required until 6 months subsequent to the issuance of this
permit, which would be December 1, 1979. This permit also re-
quired Georgia-Pacific to submit a solid waste disposal plan,
select a site for disposal of mercury, and maintain the imper-
vious asphalt covering over the mercury contaminated sludge
deposit located on Georgia-Pacific's log storage property.
The chlor/alkali plant originally discharged its mercury
treated effluent through outfall # 7. That outfall has now
been rerouted into a separate compartment in the secondary
treatment lagoon. After the pulpmill effluent has undergone
primary and secondary treatment it is combined with the chlor/
alkali effluent and both are then discharged through the sub-
merged outfall # 9.
The first NPDES permit issued for the chlor/alkali plant re-
quired stricter standards for some parameters. The daily
mercury discharge was revised from 0.2 lbs/day (0.09 kg/day)
(March 16, 1973 - December 31, 1973) to 0.1 lbs/day (0.05 kg/day)
(January 1, 1974 - December 31, 1975). The effluent was to be
free of foam or floating solids.
-27-
-------
Compared to the previous permit issued October 16, 1970, there
were also some less restrictive requirements included in the
newly issued permit (March 16, 1973). The pH of a sample was
allowed to range between 6.0 and 9.0. Mercury contained in
products produced at the plant (NaOH) was not to exceed 0.5
ppm.
Chlorine and flow standards remained at 5.0 ppm and 7.5 mgd
(28.4 mid) respectively. The mill was to continue to dispose
of chemical sludge so as to avoid contamination of State
waters.
Revisions and additions to previous permit requirements
included:
• By December 31, 1973 install facilities to continu-
ously measiure flow, temperature, chlorine residual
and pH of the effluent.
• By March 31, 11974 submit plans for pollution con-
trol during emergencies.
• Submit plans to improve diffusion of existing
outfall.
C. COMPLIANCE HISTORY
Correspondence and reports have been used here to verify a
history of Georgia-Pacific's compliance schedule to required
permit stipulations.
In order to abide with the permit stipulations for industrial
waste, primary and secondary treatment or its equivalent were
required to be operative by September 30, 1970 and June 30,
1978 respectively (Permit No. T-2862, WA-000109-1).
Operation of the primary facility began in mid-April, 1973
(Dahlgren, letter of May 1, 1973), 31 months after the original
-28-
-------
suggested compliance date. Delays in the installation resulted
from Georgia-Pacific's exploration of a joint primary treat-
ment facility with the City of Bellingham, clarifier site
objections by the Corps of Engineers, delay of a pilot lamel-
lar separator, and miscellaneous delays in the final construc-
tion. A more thorough account of the above delays has been
discussed previously in Section I.A-2.
Secondary treatment was operative by June 7, 1979 (Provost,
letter of July 31., 1979) , 11 months past the required date
(July 1, 1978) of installation. There were numerous causes for
delay; Throughout the process, DOE and EPA had difficulty
agreeing on effluent limitations and compliance dates. Fur-
ther delay resulted when Georgia-Pacific decided to use the
conventional aerated-stabilization-basin process rather than
the originally proposed Baierl Process. Once construction
commenced, Georgia-Pacific claimed problems with weather, parts
contractors, and equipment malfunctions, all of which further
postponed the completion date. Again, the schedule of events
that led to the installation of secondary treatment are
discussed more thoroughly in Section I.A-3.
Setbacks in the completion of the secondary treatment facili-
ties (required June 30, 1978) resulted in several instances of
BOD violations (Table 1-7). Final treatment facilities re-
quired subsequent to June 30, 1978 would have reduced the
number of BOD violations occurring in 1978 and 1979, since this
parameter is significantly reduced when effluent undergoes
secondary treatment.
The toxicity standards of Washington State require that 100%
of the salmonid fish tested must survive a 65% concentration
of an industry's effluent for 96 hours. This standard was
not met in Georgia-Pacific's August 26, 1974 bioassay of primary
treated bleached sulfite mill effluent (BSME). Fifty percent of
the fish died in a 38% concentration of BSME when exposed for
96 hours.
-29-
-------
Table 1-7. REPORTED SPILLS AND/OR VIOLATIONS, GEORGIA-PACIFIC MILL, BELLINGHAM BAY, WASHINGTON
Spills
Violations
Date
Amount
Source
Reference
—
chlorine
2/66 - 5/66 >
5.0 ppm (DAM)
Chlor/Alkali Plant
—
chlorine
8/67 >
5.0 ppm (DAM)
Chlor/Alkali Plant
—
mercury
unauthorized
log storage
8/24/70
2/71
N/D
N/D
Chlor/Alkali Plant
N/D
blue dye
N/D
1/06/72
N/D
N/D
chips
N/D
1/29/72
N/D
chip barge
1° effluent
N/D
stopped 1/9/74
N/D
clarifier shutdown
1° effluent
N/D
2/25/75 - 3/1/75
N/D
clarifier shutdown
isopropal
toluene
BOD
N/D
6/75 >
7/1 & 7/2/75
160,000 lbs/day
(DAM)
N/D
mill
acid tanks during
cleaning
—
SSL
1/76
N/D
N/D
—
BOD
2/76
N/D
N/D
—
SSL
2/76
N/D
N/D
—
mercury
2/76
11 lbs/day(DAM)
Chlor/Alkali Plant
NaOH
N/D
5/76
25 gallons
barge loading
—
mercury
8/76
11 lbs/day(DAM)
Chlor/Alkali Plant
—
SSL
12/75 and
1/76 - 4/76
N/D
N/D
BOD
5/76, 6/76, >
8/76
160,000 lb^/day mill
DMR 2/66-5/66
OMR 8/67
Docket #DG 70-121
District Engineer Armv Corps,
letter of 2/23/71
Dahlgren letter of 1/6/72
Reynolds letter of 1/31/72
Mowry (GP) letter of 1/11/74
Mowry (GP) letter of 2/28/75
DMR 6/75
Maverman (DOE) memo 7/10/75
Burkhalter (DOE)memo 1/10/76
Houck (EPA) letter of 2/9/76
Houck (EPA) letter of 2/9/76
DMR 2/76
Johnson (DOE) letter 5/14/76
DMR 8/76
Johnson (DOE) letter 6/10/76
DMR1s 5/76, 6/76, 8/76
Continued.
-------
Table 1-7, Page 2
Spills
Violations
Date
Amount
Source
Reference
pulp
PH
BOD
sludge
8/76 pH 9.2 N/D
(pulp 8" thick on
surface of water)
1/77- 7/77 > 110,000 lbs/day mill
(DAM)
4/16/77 small amount by-pass
Moore (DOE) letter of 8/2/76
DMR's 1/77 - 7/77
Mowry (GP) letter of 4/26/77
—
BOD
5/77 & 6/77
N/D
N/D
Lean (DOE) letter of 8/3/77
—
BOD
6/77
6 incidents
N/D
Taylor (DOE) letter of 8/8/77
—
SSL
6/77
4 incidents
N/D
Taylor (DOE) letter of 8/8/77
—
BOD
7/77
5 incidents
N/D
Johnson (DOE)letter of 9/7/77
—
SSL
7/77
3 incidents
N/D
Johnson (DOE)letter of 9/7/77
—
BOD
1/5/78
1 incident
alcohol plant
Mowry (GP) letter of 1/12/78
—
SCS
3/5/78
1 incident
N/D
Johnson (DOE)letter of 5/8/78
—
SSL
5/78 and
6/20 & 6/21/78
N/D
N/D
Johnson (DOE)letter of 8/3/78
—
BOD
6/78 - 5/79
> 31,000 lbs/day
(DAM)
1 incident
mill
DMR's 6/78 - 5/79
T-
SCS
9/26/78
faulty motor
Mowry (GP) letter of 10/18/78
Solids
N/D
1/79
1 incident
prolonged freeze
Mowry (GP) letter of 1/12/79
—
BOD
9/9/79
1 incident
clarifier station
Mowry (GP) letter of 9/7/79
—
TSS
9/9/79
1 incident
clarifier station
Mowry (GP) letter of 9/7/79
1° effluent
1° effluent
6/79-10/79
70 incidents
secondary lagoon
Mowry (GP) letter of 9/28/79
Johnson (DOE) letter of 8/23/79
Johnson (DOE)letter of 9/4/79
DAM : Daily Average/Month N/D : No data
-------
D. SPILLS AND VIOLATIONS
The discharge of any pollutant which does not conform to permit
specifications is considered to be a violation. Beginning
September 1974, all violations, bypasses, and diversions were
required by permit to be reported to DOE. Table 1—7 decribes
the documented spills and violations resulting from Georgia-
Pacific activities. Below is a list of the effluent parameters
involved in the violations:
• mercury
• log storage
• NaOH
• SSL
Mercury violations were reported on August 24, 1970 (Docket
#DG 70-121) and in March and July 1973 (Dahlgren, letters of
March and July 1973) the chlor/alkali plant could not meet
the 0.2 lbs/day (0.09 kg/day) requirement in permit T-3456
and requested a temporary variance in the permit. The
response to that request is not known.
A minor violation was brought to the attention of William
Keys of Georgia-Pacific on February 23, 1971 from the District
Engineer concerning the storage of log piles without the Corps
of Engineers approval (Corps of Engineers, letter of February
23, 1971). Again, the result of this violation is not on record.
A letter from Bruce Johnson (DOE) to enforcement offices on
May 14, 1976 reported a 25 gallon (95 liter) spill of NaOH
during barge loading operations at Georgia-Pacific. A penalty
was assessed.
Several SSL violations have been reported in the correspondence.
In a memo from Dick Burkhalter (DOE) to Bruce Johnson (DOE)
on January 19, 1976, Georgia-Pacific's monitoring reports indi-
cated a violation of daily SSL removal. On February 9, 1976
• BOD
• TSS
• sludge
• SCS
-32-
-------
a letter from Douglas Houck (EPA) to Ron Pine (EPA) reported
that Georgia-Pacific still exceeded SSL permit levels measured
by PBI. Georgia-Pacific claimed that the PBI test was not
applicable to their type of effluent. Five more incidences
of SSL violations were reported from 1976 - 1978. These and
the violations cited above can be found in Table 1-7.
Numerous BOD violations also occurred (Table 1-7). In three
incidences, the alcohol plant was determined to be the source.
The June 1977 violation was thought to be a result of a tie-
in with an alcohol plant evaporator. Failure to install secon-
dary treatment facilities resulted in the mill* s violation
(July 1978 - May-1979) of required daily average (by month)
BOD limitations (31,000 lbs/day) (14,000 kg/day). The viola-
tion on August 9, 1979 was the result of a clarifier shut-
down which also resulted in 7600 lbs (3450 kg) of TSS being
bypassed.
On May 8, 1978, a memo from Bruce Johnson (DOE) to Dick Burk-
halter (DOE) addressed enforcement action recommended for an
SCS violation that occurred on March 5, 1978. A discharge
of 65,600 lbs (29,600 kg) of SCS exceeded the permit
level of 40,000 lbs/day (18,000 kg/day). This is the only
documented occurrence of an SCS violation in DOE files.
-33-
-------
REFERENCES
Section I
Application No. 071-0YB-2-000081. June 29, 1971. From Georgia-
Pacific to the Seattle District, Corps of Engineers.
Application submitted July 28, 1978. For NP'DES permit, submitted by
Georgia-Pacific.
Behlke, James. P. April 17, 1975. Letter to Dr. Clifford Smith,
tl.S. Environmental Protection Agency.
Bellingham Herald. February 11, 1970. Page 12. "Newsweek Quote
Makes her Proud of GP%
Biggs, John A. December 3, 1976. Letter to D. DuBois, U.S.
Environmental Protection Agency, Regional Manager.
Blum, Joseph R. May 11, 1978. Letter to Colonel John A. Poteat,
Jr., Corps of Engineers, Seattle.
Britt, K.W. (ed.). 1970. Handbook of Pulp and Paper Technology.
Van Nostrand Reinhold Co. New York, n,y. 724 pp.
Burkhalter, Richard A. April 4, 1975. Letter to L. Nielson, EPA.
Burkhalter, Richard A, January 19, 1976. Letter to Bruce Johnson,
Washington State Department of Ecology.
Burkhalter, Richard A. January 23, 1978. Letter to Warren Mowry,
Environmental Control Director, Georgia-Pacific, Bellingham.
Compliance Schedule C 77-292M. May 12, 1978. To Georgia-Pacific
Corporation. Result of Order No. C 77-292M.
Corps of Engineers, Seattle, District. February 23, 1971. Letter
to William Keyes, Georgia-Pacific.
Dahlgren, Ed. October 5, 1971. Letter to Jerry Harper, DOE.
. December 21, 1971. Letter to Bruce Johnson, DOE.
January 6, 1972. Letter to Bruce Johnson, DOE.
. March 26, 1973. Letter to Bruce Johnson, DOE.
May 1, 1973. Letter to Bruce Johnson, DOE.
. July 17, 1973. Letter to Bruce Johnson, DOE.
Docket No. ijG-70-121. August 24, 1970. Issued by Washington State
Department of Ecology, Assistant Director,to Georgia-
Pacific, Bellingham.
-34-
-------
Docket No. DE 77-195. May 3, 1977. Issued by Washington State
Department of Ecology, Donald Provost, to Georgia-Pacific,
Bellingham.
Dunkak, J.H. January 26, 1972. Letter to Bruce Johnson., DOE.
. March 3, 1972. Letter to Bruce Johnson, DOE.
Georgia-Pacific Corporation, Bellingham.Daily Monitoring Reports (DMR)
submitted to DOE. 2/66-5/66, 8/67, 6/75, 2/76, 5/76, 6/76,
8/76, 1/77-7/77, 6/78-5/79.
Hallauer, Wilbur G. March 20, 1978. Letter to Henry Jackson,
United States Senate.
Houck, Douglas. February 9, 1976. Letter to Ron Pine, DOE.
Johnson, Bruce. January 12, 1972. Letter to Jerry Harper, DOE.
May 14, 1976. Letter to Enforcement Officer, Recommenda-
tion for Enforcement Action, DOE.
. June 10, 1976. Letter to Enforcement Officer, Recommehcfa-
tTon for Enforcement Action, DOE.
. July 21, 1977. Letter to Richard A. Burkhalter, DOE.
. September 7, 1977. Letter to Richard A. Burkhalter, DOE.
. May 8, 1978. Letter to Richard A. Burkhalter, DOE.
August 3, 1978. Letter to Richard A. Burkhalter, DOE.
August 23, 1979. Letter to Richard Burkhalter, DOE.
September 4, 1979. Letter to R. Burkhalter, DOE.
January 16, 1980. Personal communication to Kathy Pazera,
NEC,
Lean, Chuck. August 3, 1977. Letter to Vogel, Cameron, Provost
and Burkhalter, DOE.
Maverman, Ken. July 10, 1975. Letter to Bruce Johnson, DOE.
Moore, Allen. August 2, 1976. Letter to Bruce Johnson, DOE.
Mowry, Warren. January 11, 1974. Letter to Bruce Johnson, DOE.
February 28, 1975. Letter to Bruce Johnson, DOE.
-35-
-------
April 26,- 1977. Letter to Richard Burkhalter, DOE.
July 15, 1977. Letter to Bruce Johnson, DOE.
July 26, 1977. Letter to Bruce Johnson, DOE.
. January 12, .1978.. Letter to Bruce Johnson, DOE.
June 1, 1978. Letter to Don Provost, DOE.
June 9, 1978. Letter to Bruce Johnson, DOE.
August 7, 1978. Letter to Bruce Johnson, DOE.
October 18, 1978. Letter to Bruce Johnson, DOE.
January 12, 1979. Letter to Bruce Johnson, DOE.
September 7, 1979. Intra-company memo, Georgia-
Pacific, Beilingham, Washington.
September 28, 1979. Letter to Bruce Johnson, DOE.
Order No. C 77-292M. October 5, 1977. Notice of Motion, U.S.
District Court, Western District of Washington at Seattle,
U.S. vs Georgia-Pacific Corporation. Application for
Intervention from the Washington State Department of Ecology.
Permit No. 1861. December 18, 1962. Waste Discharge Permit
issued by the Washington State Pollution Control Commission
(WPCC) to Puget Sound Paper & Timber Company, Sulfite mill,
Beilingham.
Permit No. 1979. October 1, 1963. Waste Discharge Permit issued
by the WPCC to Georgia-Pacific Corporation, Beilingham.
Permit No. 1980. October 1, 1963. Waste Discharge Permit issued
by the WPCC to Georgia-Pacific Corporation, Tissue products
mill, Beilingham.
Permit No. 2094. October 19, 1964. Waste Discharge Permit
issued by the WPCC to Georgia-Pacific Corp., Chlorine Plant,
Beilingham.
Permit No. T-499. July 15, 1965. Waste Discharge Permit issued
by the WPCC to Georgia-Pacific Corp., Paper Board Mill,
Beilingham.
Permit No. T-2862. May 27, 1968. Waste Discharge Permit issued
by the WPCC to Georgia-Pacific Corp., Beilingham.
Permit No. 3456. October 16, 1970. Chlorine Plant permit
issued by DOE to Georgia-Pacific Corporation.
-36-
-------
Permit No. T-3456. March 16, 197 3. NPDES Permit issued by
DOE to chlorine plant, Georgia-Pacific Corp., Bellingham.
Permit No. WA -000109-1. NPDES Permit from DOE for the Georgia-
Pacific pulpmill. Issued May 13, 1975; Re-issued June 1,
1979.
Permit No. WA-003039-2. February 16, 1977. NPDES Waste Dis-
charge Permit issued to Georgia-Pacific Corp., Chlor/
Alkali Plant, Bellingham.
Provost, Donald 0. May 13, 1975. NPDES Waste Discharge Permit
issued to Georgia-Pacific.
July 14, 1976. Letter to Ed Dahlgren,
. March 9, 1977. Letter to Warren Mowry, Georgia-Pacific,
Bellingham.
. May 10, 1977. Letter to Warren Mowry, Georgia-Pacific,
Bellingham.
. July 31, 1979. Letter to John A. Biggs, DOE.
Reynolds, V. January 31,1972. Inter-departmental communication
to Georgia-Pacific files.
Smith, Dr. Clifford A. April 11, 1975. Letter to J. Biggs, DOE.
. April 29, 1975. Letter to J. Behlke, DOE.
Stanley, Roger. August 3, 1979. Letter to Georgia-Pacific files.
Stipulation No. 867. Pollution Control Hearing Board. November 23,
1976. State of Washington. PCHB. Georgia-Pacific vs. State of
Washington Department of Ecology.
Taylor, Lloyd. August 8, 1977. Letter to Georgia-Pacific. Notice
of Penalty Incurred and Due.
Washington State Department of Ecology. March 19, 1972.
Pact Sheet; Technical Information. Georgia-Pacific, Bellingham.
Washington State Department of Ecology. March 17, 1975. Georgia-
Pacific Tentative Compliance Schedule for NPDES Permit.
-------
II. INDUSTRIAL AND MUNICIPAL EFFLUENTS AND
COMPOSITION
In the past 13 years (1966-1979) Bellingham Bay has been the
receiving waters for processed industrial, municipal and domestic
wastes. This chapter provides information on the facilities con-
tributing to these waste waters and a brief description of the
effluent constituents. Section A provides a brief overview of
the major industrial flows to Bellingham Bay including a quanti-
tative and qualitative discussion of effluents discharged by the
Georgia-Pacific and other industrial and municipal facilities.
Section B provides a chronological listing of Georgia-Pacific's
shutdowns. This is followed by a discussion in Section C on the
known toxic constituents contained in the effluent from bleached
sulfite pulping process both generally and from the Georgia-
Pacific mill.
A. EFFLUENT DISCHARGES
The receiving waters of the study area are divided into Inner
Bellingham Bay (Class B) and Outer Bellingham Bay (Class A)
(Figure II-l). The standards and criteria for these classifica-
tions are discussed in Chapter IV, Section A. In order to devise
a complete inventory of discharges to Bellingham Bay (Class A and
B waters), facilities discharging to tributaries flowing into the
Bay north of Post Point have also been indicated. The direct
receiving water of each discharging source is indicated (Table
II-l); however, Bellingham Bay is the final receiving water in
most cases.
Excluding ground discharging facilities, a minimum of 23- industrial
or municipal facilities are presently known to discharge industrial
processed or unprocessed waste, treated municipal or domestic
sewage, or non-contact cooling water to Inner and Outer Bellingham
Bay (Table II-l, Figure II-2) . The sulfite pulp and paper
industry (Georgia-Pacific), chlorine production facilities (Georgia-
Pacific) , and municipal facilities (Bellingham Sewage Treatment
Plant (STP)) contribute the major process waste flows to
-38-
-------
Belllngham Is
4000
1000 2000
500 1500
3000
Hooka actc
River
Lummt
Indian
Reservation
Bellingnam
Bay
Portage
Chuckanut
Bay
Luimnf i4l,
Governors
Point
Figure II-l WASHINGTON STATE DEPARTMENT OF ECOLOGY WATER
CLASSIFICATIONS AT BELLINGHAM BAY.
Source: DOE 1978
-39-
-------
Table II-l KNOWN SURFACE HATER AND GROUND DISCHARGE SOURCES IN THE BELLINGHAM BAY AREA (See Figure II-2)
Map
Key
Facilities
Began
Discharge
Ceased
Discharge
Discharge Type
Previous
Receiving Waters
Present
1 A&M By-Products Co.
2 Bellingham Cold Storage Co.
3 Bellingham Frozen Foods
4 Bellingham Hatchery
Bellingham STP
5 »c" Street Plant
6 Post Point Plant
7 Bellingham Water Treat-
ment Plant
8 Birchwood Farms, Inc.
9 Bornstein Seafoods, Inc.**
10 Bumble Bee Seafoods
11 Columbia Cement Co.
12 Consolidated Dairy
Products Co.
13 Crispy Corn Co.
14 Dahl Fish
-------
Map
Key
20
21
22
23
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
39
Table II-l Continued
Facilities
Began
Discharge
Ceased
Discharge
Discharge Type
Receiving Waters
Previous•
Present
Georgia-Pacific Chlorine Plant 1965*
Kelley Farquhar Co. (Bell.) June 1968*
Kelley Farquhar Co. (Ferndale) May 1967*
Lake Whatcom Hatchery
Lummi Fish Hatchery
Lynden STP
Lynden Transport
Lynden Water Treatment Plant
Mt. Baker Jr.Sr. High School
Mt. Baker Plywood, Inc.
Nooksack Fish Hatchery
Oesar Cedar Co.
Olivine Corporation
Pacific Concrete Industries
R.G. Haley Intern. Corp.
Schenk Seafood Sales, Inc.
Seabrook Farms Co., Inc.
Sea-Pac Co., Inc.
1965**
1973**
1934
1973**
1924*
1974**
March 1965
1965**
March 1963*
1973**
April 1973*
Sept. 1952*
August 1962*
August 1966*
June 1968*
Sea West Industries, Inc. January 1971*
Shuksan Frozen Foods, Inc. August 1966*
N/A Industrial Wastewater
N/A Industrial Wastewater
N/A Industrial Wastewater
Non-contact cooling water
N/A Industrial Wastewater
N/A Industrial Wastewater
N/A Municipal
N/A Industrial Wastewater
N/A Municipal
N/A Domestic
N/A Industrial Wastewater
non-contact cooling
water
N/A Industrial Wastewater
N/A Industrial Wastewater
N/A Industrial Wastewater
N/A Industrial Wastewater
N/A Industrial Wastewater
Non-contact cooling water
N/A Industrial Wastewater
N/A Industrial Wastewater
N/A Industrial Wastewater
Non-contact cooling water
N/A Industrial Wastewater
N/A Industrial Wastewater
Inner Be11. Bay
Bellingham Bay
Nooksack River
Nooksack River
Lake Whatcom
South Fork of
Nooksack River
Nooksack River
Fishtrap Creek
Nooksack River
Ground
Bellingham Bay
Bellingham Bay
Nooksack River
Little Squalicum
Creek
Inner Bell. Bay
Ground
Ground
Inner Bell. Bay
Inner Bell. Bay
Nooksack River
Inner Bell. Bay
Inner Bell. Bay
Bellingham Bay
Nooksack River
Bellingham Bay
Bellingham STP
Ground
Nooksack River
Lake Whatcom
South Fork of
Nooksack River
Nooksack River
Fishtrap Creek
Lynden STP
Ground
Bellingham STP
Bellingham Bay
Nooksack River
Bellingham STP
Inner Bell. Bay
Ground
Ground
Inner Bell. Bay
Bellingham STP
Lynden STP
Bellingham STP
Inner Bell. Bay
Bellingham STP
Lynden STP
continued
-------
Table II-l Continued
Map
Began
Ceased
Receiving
Waters
Key
Facilities
Discharge
Discharge
Discharge Type
Previous
Present
40
Van Werven Trucking Co.
1973**
N/A
Industrial Wastewater
Ground
Ground
41
Whatcom County PUD #1
October 1966*
N/A
Municipal
Nooksack River
Nooksack River
42
Whatcom County Infirmary
1930's
N/A
Domestic
Silver Creek
Silver Creek
43
Wilder Construction
1974**
N/A
Industrial Wastewater
Ground
Ground
*
Based on available permit and/or application on file at DOE, Northwest Regional Office, Redmond, Washington.
Initial operation of the facility may be earlier than indicated.
*
Earliest data found in available reports. Initial operation of the facility may be earlier than indicated.
I
N>
I
-------
J Figure II-2 HISTORY OF THE KNOWN INDUSTRIAL AND MUNICIPAL DISCHARGE.LOCATIONS |
I OF BELLINGHAM BAY I
-------
Bellingham waters. Minor waste flows to the study area are
discharged from industries involved in rock crushing (Olivine
Corporation), concrete (Columbia Cement), truck hauling (Lynden
Transport), fish production (Bellingham, Lake Whatcom, Lummi and
Nooksack Fish Hatcheries), and municipal or sanitary waste
treatment (Everson, Ferndale, . Lynden STPs, Whatcom County PUD #1
and Whatcom County Infirmary).
Discharged waste waters from Georgia-Pacific contain suspended
solids (SS), inorganic constituents, and concentrations of
organic material measured as biological oxygen demand (BOD). In
addition to the manufacture of pulp and paper, Georgia-Pacific
commercially produces chlorine and caustic soda in their chlor/
alkali plant. Mercury and chlorine are the major waste water
products from this facility.
The municipal sewage treatment plants contribute chlorine,
bacteria, organic nutrients and solids to the receiving waters.
Suspended and settlable solids are the main waste water con-
stituents in effluent flows from minor industries. In addition
to solids, hatcheries also discharge ammonia nitrogen to
receiving waters (CH2M Hill, May 1974).
During the past 13 years (1966 - 1979) Georgia-Pacific has been
the leading contributor of industrial waste flows to Bellingham
Bay, averaging 40.9 mgd (154.8 mid). The maximum flow from the
mill occurred in 1974 (48.04 mgd (181.83 mid)). The Georgia-
Pacific Chlorine Plant (1966 - 1967 and 1976 - 1979) and the
Bellingham STP (1972 - 1979) contributed daily effluent flows
of 18.69 mgd (70.74 mid) and 7.60 mgd (28.77 mid), respectively.
The remaining industries and municipal facilities discharged
an average of 0.73 mgd (2.76 mid) and less (Table II-2).
-44-
-------
Table II-2 AVERAGE ANNUAL DISCHARGES OF WASTE WATER TO BELLINGHAM BAY 1966-1979
Haste Source
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975 1976 1977 1978
1979 1900
ASH Products Co.**
.005
.005
.005
.01! 5
.005
.005
.005
.005
N/D
N/D N/D N/D .005
.006
Bellingham Cold
| Industrial Wastewater to Bellingham STP
-
Storage Co.**
.340
N/D
N/D
.200
.340
.340
.340
N/D
. 158
.094cw ,094cw .094cw .095cw
,095cw
Bellingham Frozen
Indue
trial Wastewater to Bellingham STP
Fooda**
N/D
N/D
1.150
1.150
1.150
1.150
1.150
N/D
J.37
N/E N/E N/E N/E
"N/E
Bellingham Hatchery
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D N/D N/D N/D
N/D
Birchwood Farms Inc.
No permit required.
Bornstein Seafoods
| Industrial Wastewater to Bellingham STP
Inc.**
N/D
N/D
.520
.520
.520
.357
. 157
N/D
.111
.006cw .006cw .006cw .006cw
. 0C6trw
Bumble Bee
Industrial Wastewater to Bellingham STP
*a »• •* • »
.ISOcw ,150cw .150cw .IdOcw
Seafoods
.291**
.291**
.097**
.097**
.097**
.450
.450
N/D
N/P
.150cw
Columbia Cement Co.
.200**
.200** .200**
.200**
.200**
.200"
.256**
.256**
.197*
.067
.069
.067
.062
.050*
Consolidated Dairy
Products Co.
Industrial Waste-
water to Lynden STP
N/D
N/D N/D
N/D
N/D
1.40**
1.40**
N/D
.613*
.682*
.755
.635
.762
l.Ocw
Crispy Corn Co.
No permit
required.
Dahl Fish Co.
Inc.**
Industrial Waste water
to Bellingham STP
.005
.005 .077
.077
.077
.077
.077
N/D
.048
.048
.048
.048
.024cw
.024cw
DeJong Packing Co.**
N/D
.010 .010
.010
.010
.010
.010
.028
.028
.028
.028
.028
.030
.030
Everson Canning Co.
No permit
required.
Ferry Brothers Inct*
N/D
N/D N/D
N/D
N/D
N/U
N/D
N/D
N/D
N/D
N/D
N/D
.005
.005
Georg ia-Pacific
Sulfite Mill
32.IB*
33.B7* 35.70*
41.43*
45.36*
45.50
46.17
43.71*
48.04
42
.70
41.47
41.98
36.45
37.04*
Georgia-Pacific
Chlorine Plant
2.83
3.70 N/D
H/D
N/D
N/D
N/D
N/D
N/D
N/l>
6.32*
b. 45
6.50*
6.15*
Kelley Farquhar
and Co.**
(Bellingham)
Industrial Waste water
to Bellingham STP
N/D
N/D 1.03U
1.038
1.038
.830
.830.
N/D
.798
N/1>
N/E
N/E
N/E
N/E
Kelley Farquhar
and Co.
(Ferndale)
| Industrial Waste Water to Ground
1.392**
1.392** 1.392**
1. 192**
1.220**
1.220**
1.220**
1.265**
.731*
283
.461*
*»
.150cw
**
.150cw
**
. 750C«
-------
Table II-2, Page 2
1966
1967
1968
1969
1970
1971
197U
1973
1974
197b
1976
1977
1978 1979 1980
Lake Whatcom Hatchery
No Permit required.
Lynden Transport
No Permit required.
Lummi Fish Hatchery
No Permit required.
Mount Baker
Plywood Inc.
Industrial Waste Water to Bellingham STP
M/D
N/D
N/D
N/D
.100**
. 100**
.100**
N/D
.124*
.109
N/D
N/D
N/D N/D
Nooksack State
Salmon Hatchery
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
-N/D
N/D
:005
.004
.006 .005
| Industrial
Waste water
to Bellingham STP
Oesar Cedar Co. **
.010
.010
.014
.014
.014
.014
.014
.014
N/D
N/ |!
N/E
N/E
N/E N/E
Olivine Corp.**
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
.005
.005
.005
.005 .005
Pacific Concrete
Industries**
.060
.068
.144
.144
.144
.144
.144
N/D
N/D
N/D
N/D
N/D.
N/D N/D
R.G. Haley Interna-
tional Corp.**
.048
.048
.048 .048 .018 .048 .(I4H .04fi
Scheuk Seafood
Sales Inc.**
.U30cw .007cw .OOHcw .OOUcw .007cw .006cw
[ Industrial Waste water to Bell STP
N/0
N/0
N/O
N/D
N/O
.(HI I
• OAS . UHS
.OBS N/l) N/n N/E
N/E
N/E
Seabrook Farms
Co, Inc. .140* N/D .090** .090** .090** .275** .275** N/0
Indus. WW to
Lynden STP
.339*
.307*
.100
.126
H/P
.302*
Seawest
Industries Inc.**
1 1
I Industrial
Waste water
to Bellingham STP
N/0
N/D
N/D
N/D
N/D
.029
.029
.029
.029
029
N/E
N/E
N/E
N/E
Industrial
Waste water
to Bellingham STP
Sea-Pac Co., Inc.**
N/D
N/D
.014
.014
.014
.014
.014
N/D
.014
N/D
N/D
N/D
.OOScw
_ _ _ •#
.OOScw
Shuksan Frozen
Foods, Inc. **
Indus. WW to
Lynden STP
.075
.075
.075
.075
.075
.075
.075
N/D
N/D
N/D
N/D
N/D
N/0
N/E
Van Herven Trucking
~ Co.
No permit required
Milder Construction
No Permit required
-
-------
Table Hr2, Page 3
Municipal Waste
Source
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979 1980
Bellingham STP
"C" St. Outfall
N/D
N/D
N/D
N/D
N/D
N/D
6.22*
6.50*
7.70*
Post Pt. Outfall
5.22*
8.36
5.48
6.44
7.49
7.38
Bellingham Water
Treatment Plant
Waste
Water to Bell. STP
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
.191*
.163*
N/D
N/E
Everson STP
N/A
N/A
N/A
N/A
N/A
N/A
N/A
.065*
.063
.072
.070
.070
.070*
.070*
Perndale STP
N/A
N/A
N/A
N/A
N/A
!J/'D
N/D
N/D
N/D
N/D
. 54* "
.51
.52*
.47*
Lynden STP
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
.44
.44*
.43
.49*
1.05*
Lynden Water
Treatment Plant
I Waste
Water to Lynden STP
N/D
N/D
N/D
N/D
H/U
M/U
N/D
N/D
N/l)
N/D
.030**
.030**
.030**
N/E
Mt. Baker Jr. Sr.
High School No permit required.
Whatcom County
Infirmary No permit required.
Whatcom.County
PUD IX N/D N/D N/D N/D N/D N/D N/D N/D N/D N/D .383** .53 .02 .01*
*
Daily average obtained from available DMR's representing less than a 12 month period. N/D - No available data
Maximum available daily average flows stipulated by permit. ™ cooling water ¦
N/E - No effluent discharged to Bellingham Bay
N/P - No processing
-------
In addition to flow, the Georgia-Pacific mill is also the main
contributor (1967-1979) of suspended solids (SS). Primary
facilities operational by April 1973 reduced the mill's SS dis-
charge; however, Georgia-Pacific remains the major contributor
of this waste to the Bay. Subsequent to the operation of secon-
dary facilities (June 1979), the mill's discharge of BOD was
reduced from 78,000 lbs/day (35,000 kg/day) (January - May 1979)
to 21,000 lbs/day (9,500 kg/day) (June-August 1979). Prom July 1-
November 30, 1979 the Bellingham STP was allowed a BOD discharge
of 40,000 lbs/day (18,000 kg/day) (Cameron, Order Docket No.
DE 77-376 of July 19, 1977); therefore, during this time.period
the Bellingham STP became the major source of BOD to the study area.
1. Georgia-Pacific
Previous to 1975, Georgia-Pacific was required by permit to
submit daily monitoring reports (DMR) on specific effluent
characteristics to the Washington Pollution Control Commission
(WPCC)/ predecessor to the Washington Department of Ecology
(DOE). Upon issuance of Georgia-Pacific's first National
Pollution Discharge Elimination System (NPDES) permit (WA
000109-1) on May 13, 1975, the mill began to submit effluent
reports to DOE. Available DMR's (1966 - 1979) for Georgia-
Pacific provide information on seven effluent characteristics
(flow, production/ TS, TSS, SCS, BOD and Ca-SWL). The fre-
quency and type of sampling for each parameter is determined
according to permit requirements. The following material
provides an analysis of each parameter in regards to discharged
quantities and permit requirements.
Early Georgia-Pacific permits (1968-1973) specified a maximum
waste flow (51.4 mgd (194.6 mid))(Permit No. T-2862); however,
subsequent to May 1975 there were no flow restrictions included
in the permit except for monitoring and inclusion in the DMR
(Figure II-3) . From 1966 until April 1973, these flows were
monitored on outfalls from the hydraulic barker (2), alcohol
plant (3), blow pits (4), bleach plant (5) and the chemical
-48-
-------
60
55
50
45
40
3 35
30
25
20
,a
-------
groundwood plant (CGW). Upon completion of the primary treatment
facilities (April 1973), mill flow was obtained from outfalls
3, 5 and the primary clarifier. Effluent from the primary clari-
fier was monitored separately from its outfall location (5);
however, it should be made clear that Georgia-Pacific discharged
pulp wastes from only two outfall locations (3 and 5) after April
1973 (see Section I.A.I.). From June 1975 to June 1979, flow
reports were derived from pipes 3f 5 and 8. Discharge 8 had been
operative since 1945, but monitoring was not initiated until
the summer of 1975. By June 1979, all monitored discharging
pipes from the pulp mill (3 and 5), municipal storm sewer line (8)
and chlorine plant (7) were rerouted and combined to form Pipe
9. Required monitoring has been conducted on the total discharge
from this outfall since June 1979.
Georgia-Pacific was required to install primary facilities by
September 30, 1970 (Permit No. T-2862) to remove all floating and
settlable solids. Daily monitoring reports subsequent to pri-
mary treatment installation (April 1973) show a definite decrease
in SCSand slightly depressed levels of TS. From 1966 - April
1973, monthly averages for SCS and TS averaged 31,220 lbs/day
(14,160 kg/day) and 834,250 lbs/day (378,420 kg/day), respectively
(Figures II-4 and II-5). These monthly averages were decreased
to 16,470 lbs/day (7470 kg/day) (May 1973 - September 1978) for
SCS and 580,833 lbs/day (263,466 kg/day) (May 1973 - May 1975)
for TS (Figures II-4 and II-5). Both parameters were monitored
from outfalls 2, 3, 4, 5, and CGW, which were combined into the
two sources (3 and 5) by April 1973. Beginning in June 1975
the mill monitored one additional outfall (8), but SCS levels
did not increase significantly.
Secondary facilities were operative at Georgia-Pacific by June 7,
1979, resulting in an 11 month (July 1, 1978 - June 1979) vio-
lation period. During this time average BOD waste loads
(79,500 lbs/day (36,100 kg/day)) exceeded the required monthly
average of 31,000 lbs/day (14,000 kg/day) by approximately
156 percent (Figure II-6). Previous violations of BOD permit
-50-
-------
a
2 7 , 00
I
I 20
Hit
Figure
II-4 GEORGIA-PACIFIC MONTHLY AVERAGE FOR SUSPENDED COMBUSTIBLE SOLIDS (SCS)
-------
MITmTTT!
T!
•n;
1 300
Figure I1-5 GEORGIA-PACIFIC MONTHLY AVERAGE FOR TOTAL^SOLIDS (TS)
-------
2 I
300
270
240
210
1180
* I *
iec
>150
120
10
90
60
30
.S4|^<«OK
-IKKIiKOOXI
t«kS4ca^n<«0;
1979
1980
1979
1974
1970
1969
1967
Figure II-6 GEORGIA-PACIFIC MONTHLY AVERAGE FOR BIOLOGICAL OXYGEN DEMAND (BOD)
-------
standards occurred from January 1977 to July 1977, indicating
that failure by the mill to install the required facilities
caused non-compliance with the permit BOD levels (Figure II-6).
A comparison of TSS values shows an increase of roughly 50 percent
after the aerated stabilization basin (ASB) was installed
(Figure -II-7) . This expected elevation is a direct result of the
effluent's 6-7 day retention period in the ASB, which contains
bacterial sludge. A number of bacteria remain suspended
in the discharged effluent, producing elevated TSS levels.
Therefore, increases in permit levels have been made (No. WA-
0000109-1, June 1, 1979) (Johnson, personal communication on
January 22, 1979).
Monitoring of spent sulfite liquor was not required after June 30,
1978 (Permit No. WA 0000109-1). As a result, the effects of
I
Georgia-Pacific secondary treatment facilities on this parameter!
cannot be examined (Figure II-8).
The second largest contributor of industrial waste water to the
Bay is the Georgia-Pacific chlor/alkali plant, which began
operation in 1965 (Georgia-Pacific, October 1972) (Table II-l).
The process waste water from the plant is contaminated with
mercury derived from the mercury cell process used to produce
chlorine and caustic-soda (Fiedler, letter of April 4, 1974).
In order to reduce discharged mercury in the effluent, a re-
covery and reuse system and a mercury sulfide system were in-
stalled by July 1970 and December 1973 respectively (Fiedler,
letter of April 4, 1974).
Correspondence indicates that previous to July 1970 the Chlor/
alkali plant discharged approximately 10.2 lbs/day (4.6 kg/day)
of mercury, which was reduced to 0.20 lbs/day (0.09 kg/day)
(monthly average) after treatment was installed (Fiedler, letter
of April 4, 1974). Despite the fact that the plant was required
to monitor and report their mercury output (beginning October
16, 1970), there are no available DMR's containing mercury
-54-
-------
r*v
«
i
s«
3f|
•O I
50
AO
U
45
ui
TT1
liill
mKIiKNOK -M.|4g-%-k*ttOX£ -MkS4a**~><*OS( -ntl<|ii0«|
»i4r>i««on uKittooi
nfcKlnwoi
1979
IMP
1878
1975
1977
1973
1968
1971
Figure
II-7 GEORGIA-PACIFIC MONTHLY AVERAGE FOR TOTAL
SUSPENDED SOLIDS (TSS)
-------
rnnrrn
•m
a!
M
CT> 1.0
fj*"i
Fiqure II-8 GEORGIA-PACIFIC MONTHLY AVERAGE FOR SPENT SULFITE LIQUOR (SSL)
-------
monitoring results to verify the cbirrespondence or indicate
if the 0.2 lbs/day (0.09 kg/day) monthly average was maintained
through December 1973. Subsequent to December 31, 1973 the mill
was required to reduce mercury discharge to 0.10 lbs/day (0.05
kg/day) (monthly average). Again correspondence indicates that
this was achieved (Fiedler, letter of April 4, 1974), but a lack
of monitoring reports on monthly mercury averages does not allow
verification of compliance.
Beginning in January 1976 available monitoring reports provide
the monthly average of mercury contained in the effluent from
the chlor/alkali plant (Figure II-9). Technically, Permit
No. T-3456 issued March 16, 1973 expired December 31, 1975;
however, since there was no permit issued between December 1975
and February 16, 1977, the plant was required to abide by the
expired permit (No. T-3456). Using the 0.10 lbs/day (0.05 kg/
day) monthly average limit, only 2 mercury violations occurred
(February and August 1976) from January 1976 to May 1979
(Figure II-9). During this time the average daily mercury
discharge for the year decreased from 0.08 lbs/day (0.04 kg/day)
(1976) to 0.02 lbs/day (0.01 kg/day) (January - June 1978).
Chlor/alkali permits issued from 1964 to 1979 required the plant
to monitor chlorine and submit the results to the appropriate!
agency (WPCC previous to October 1970, DOE subsequent to Novem-
ber 1970). The DMR's are incomplete and only provide sporadic
monitoring results. Utilizing the limited reports, the only
known violations occurred in 1966 and 1967 (February 1966 -
May 1966, and August 1967) (Figure 11-10).
2. Other Industrial and Municipal Dischargers
In addition to the Georgia-Pacific pulp and paper mill and
chlorine plants, a minimum of 23 industrial and 8 municipal
facilities discharged process wastes to Bellingham Bay by May
1974* Installation of a new sewage treatment plant at Post
-57-
-------
20
0.10
0.10
.10
.08
•m
U1
CO
.04
.02
KIiKMOK HkJOn
tC ^XaiMNOXI
.|4|lM«OS(
1976
1977
1978
1979
1974
I960
1971
1973
1970
Figure II-9 GEORGIA-PACIFIC CHLORINE PLANT MONTHLY AVERAGE FOR MERCURY
-------
10
3:q
3.0
35
•ul
Ul
VD
-M.a^a-*n«oOzc ¦»»li4«OU
^Klnt^K iik|
-------
Point: (Bellingham STP, September 1974) provided primary treat-
ment facilities for processed industrial waste water. By
Spring 1978, 11 industries diverted their process wastes to the
Bellingham STP (Garner, letter of February 6, 1980) (Table II-3).
Additional facilities (industrial and municipal) diverted process
wastes to Lynden (4 facilities) or Bellingham (1 facility) sewage
treatment plants by the Spring of 1979 (Tables II-3 and II-4) .
Excluding the Georgia-Pacific facilities, these diversions coupled
with the closure of Everson Canning in 1978 produce a present
total of 15 industries and 7 municipal facilities discharging to
Bellingham Bay (Tables II-3 and II-4).
The remainder of this section is divided into categories repre-
sentative of specific facilities known to discharge to Bellingham
Bay as of May 1974 (303e Staff, October 1975 and CH2M Hill i974).
The categories include the following facilities: food processing
(fiish, vegetables, and fruits) , fish culture, wood processing,
miscellaneous industries and municipal.
Food Processing: There are twelve food processing related indus-
tries discharging to waters in the Bellingham Bay area (Tables II-l,
II-3). Only four of these industries operate on a year round basis
(Bellingham Cold Storage, Bornstein Seafoods, pahl Fish, and
Seawest Industries). The remaining food processors operate between
the months of June and December. The daily averages per year for
all industries represent only the operative months for respective
years (Table II-2).
Comparing the three food processors discharging to the Nooksack
River (Kelley Farquhar, Seabrook Farms and Shuksan Frozen Foods),
Kelley Farquhar discharged the highest quantity of cooling water
(.75 mgd (2.84 mid)) for 1979 (Table II-2). Previous to the
diversion of processed waste to the Lynden STP (Seabrook Farms
and Shuksan Frozen Foods) or to the ground (Kelley Farquhar) all
vegetable and fruit water (passed through 20-30 mesh screen,
removing solids) was discharged to the Nooksack River. Presently
-60-
-------
Table II-3 SUMMARY OP SURFACE HATER INDUSTRIAL DISCHARGE SOURCES AND DIVERSIONS TO SEWAGE TREATMENT PLANTS
Discharged to Bnllinqham Bay
Presently discharging to
D1 anf
Before May 1974
Be 11Ingham Bay
riaiii
(Final Receiving Waters)
(final Receiving Waters)
Process Waste Diverted to:
Type of
Operation
Average
Non-contact Industrial
Mon-contact Industrial
Bellipghaja
Lynden
Industrial Facilities
Industry
Oays/Vear
Cooling Water Waste Water
Cooling Water Waste Water
STP
STP
Ground
BellIngham Cold Storage Co.
Seafood Processing
Year Round
e e
e '
July 1975
N/A
N/A
Bellingham Frozen Foods
Vegetable Processing
150
•
June 1974
N/A
N/A
Bellinyham Fish Hatchery
Fish Culture
Year Round
• N/P
•
N/A"
N/A
N/A
Bornstein Seafoods, Inc.
Bottom Fish
Year Round
• •
•
March 197S
N/A
N/A
Processing
Bumble Bee Seafoods
Salmon.Processing
ISO
• •
••
Sept. 1975
N/A
N/A
Columbia Cement Co.
Manufacture concrete
Year Round
•
e
N/A
N/A
N/A
Consolidated Dairy
Powdered Milk
Year Round
e •
N/A
Fall 1978
N/A
Products - Oar190Id
Products
Dahl Fish Co. Inc.
Fish Processing
Year Round
• •
•
Spring 1978
N/A
N/A
Everson Canning Co.
N/0
N/O
• •
closed 197B
N/A
N/A
N/A
Kelley Farquhar Co.
Vegetable Processing
130
•
July 1975
N/A
N/A
(Bellingham)
Kelley Farquhar Co.
Vegetable Processing
180
• •
e
N/A
N/A
Summer
(Ferndale)
1977
Lake Whatcom Hatchery
Fish Culture
90
• N/P
•
N/A
N/A
N/A
Lynden Transport
Truck Hauling
Year Round
•
•
N/A
N/A
N/A
Mt. Baker Plywood, Inc.
Plywood & Veneer
Year Round
• e
•
Feb. 1976
N/A
N/A
Nooksack Fish Hatchery
Fish Culture
Year Round
e N/P
e
N/A
N/A
N/A
Oesar Cedar Co.
Hood Preserving
Year Round
•'
Oct. 1975
N/A
N/A
Olivine Corp.
Rock Crushing
Year Round
•
e
N/A
N/A
N/A
R.G. Haley Int. Corp.
Hood Preserving
Year Round
e
e
N/A
N/A
N/A
Schenk Seafood Sales Inc.
Salmon Processing
ISO
e
Sept. 1977
N/A
N/A
Seabrook Farms Co. Inc.
Vegetable Processing
100
N/A
Spring
1979
N/A
Seatiest Industries, Inc.
Seafood Processing
Year Round
e
July 1975
N/A
N/A
Sea-Pac Co. Inc.
Salmon Processing
100
e •
e
May 1977
N/A
N/A
Shuksan Frozen Foods, Inc.
Fruit Processing
56
e
N/A
Spring
1979
N/A
Lumni Fish Hatchery
Fish Culture
N/D
e
' e
N/A
N/A
N/A
* Also contains water used to flume salmon from fish boats to salmon bine:. N/D - No data N/A - Not applicable
** Late 1979 diverted solids to Bellingham STP N/P - Not processed
-------
Table II-4 SUMMARY OF MUNICIPAL DISCHARGE SOURCES AND DIVERSIONS TO SEWAGE TREATMENT PLANTS
Discharge to Presently Dis-
Bellingham Bay charging to Process Waste Process Waste
Waters by Bellingham Bay Diverted to Diverted to
Municipal Facilities
May 1974
waters
Bellingham STP
Lynden STP
Bellingham STP
•
•
N/A
N/A
Bellingham Water Treatment
Plant
•
October 1978
Everson STP
•
•
Ferndale STP
•
•
Lynden STP
•
Lynden Water Treatment Plant
•
1978
Whatcom County PUD #1
•
•
Whatcom County Infirmary
•
i
cn
K)
I
-------
only Kelley Farquhar continues to discharge non-contact cooling
water to the Nooksack River. The Everson Canning Company closed
in 1978; however, during operation in the 1970's all process
waste water was diverted to a non-overflow lagoon. Non-contact
cooling water was diverted to the Nooksack River.
The remaining nine food processing industries are a combination
of vegetable and seafood or fish processors (Table II-2). Kelley
Farquhar in Bellingharo and Bellingham Frozen Foods (vegetable
processors) divert all waste water through a screen subsequent to
discharge to Bellingham STP. The seafood and fish processors
are required to divert all wash water through a % inch mesh
screen or smaller prior to discharge to the STP. From the late
1960's until their hookup to the Bellingham STP, both the vegetable
and seafood industries utilized the solids-screening process
before discharging to the Bay.
Sea-Pac, Dahl Fish, Bumble Bee, Bornstein and Bellingham Cold
Storage are the only seafood-fish processors continuing to
discharge (non-contact cooling water) to the Bay since diversion
of industrial food processing waste (9 industries) to Bellingham
STP (Table II-3) . In addition to non-contact cooling water,
Bumble Bee continues to discharge to the Bay fluming water used
to wash salmon from the fish boats into salmon bins.
Fish Culture: The Bellingham and Nooksack Fish Hatcheries are the
only two fish culture facilities in the study area requiring an
NPDES permit. The Lake Whatcom Fish Hatchery spawns land locked
salmon (Kokanee) from Lake Whatcom (Gearherd, personal communica-
tion of January 17, 1980).
The Lummi Fish Hatchery maintains a salmon hatchery which spawns
the coho, chum and Chinook species. Processed water from the
Lummi Hatchery is recycled and then diverted to settling ponds
before being discharged to the South Fork of the Nooksack (CH2M
Hill 1974). Three hatcheries (Bellingham, Nooksack and Lake
Whatcom) maintain a one-time flow-through system which allows
-63-
-------
untreated effluent to be discharged to the receiving waters
(CH2M Hill 1974). Untreated effluent (food and fish waste pro-
ducts) from the hatcheries contains ammonia nitrogen and is
similar to sewage effluent from a secondary treatment facility
(CH2M Hill 1974).
The main waste problem of hatcheries involves the disposal of
accumulated solids from the rearing ponds. By 1973 and possibly
earlier the Nooksack and Lummi Fish Hatcheries annually vacuumed
the solids from rearing ponds and buried the waste on land
(CH2M Hill 1974). Presently, the Nooksack Hatchery removes solids
from the rearing ponds on a regular basis (Peck, person correspon-
dence of February 7, 1980).
The Bellingham Hatchery continued to discharge rearing pond
solids to Whatcom Creek until late 1979 (Gearherd, personal
communication of February 11, 1980). At this time, a vacuum
system was installed to pulp sediment from the rearing pond into
a holding pond for dewatering. The supernatant (water above the
settled solids) from this process is discharged to the receiving
water and the sediments are diverted to the Bellingham STP
(Gearherd, personal communication of February 11, 1980).
The Lake Whatcom Hatchery, a kokanee fry raising station, is not
required to operate according to a state or federal discharge
permit. Compared to the other three hatcheries, the fry station
utilizes a minor amount of feed and retains the fish for shorter
time periods; therefore, waste in the effluent is decreased.
Solids from the Lake Whatcom rearing ponds continue to be dis-
charged into the receiving waters (Gearherd, personal communica-
tion of February 11, 1980) .
Wood Related Industries: R.G. Haley is the only wood processing
industry presently discharging (non-contact cooling water) to
Bellingham Bay (Table II-3). Available information indicates
that since 1971, R.G. Haley discharged all contaminated waste to
a holding tank or sump which was trucked off-site for disposal.
-64-
-------
Previous to fall 1975, both R.G. Haley and Oesar Cedar Company
discharged to the Bay; however, only Oesar Cedar discharged indus-
trial waste water containing phenol and oil. Permits on file at
00E (No. 2900) indicate an allowable maximum of 5 ppm phenol and
10 ppm total oils. By October 1975, Oesar diverted all processed
waste water to the Bellingham STP.
From 1970 until fall 1975 Mount Baker Plywood utilized a lagoon
and sump for settling of solids and glue wastes, respectively. Upon
completion of proper industrial treatment facilities, all process
industrial waste water was directed to Bellingham STP (February
1976) (Table II-3).
Miscellaneous Industries: By 1973 and possibly earlier, Consoli-
dated Dairy discharged wash water from the milk process, truck
wash, and floor drains into the Nooksack River (DOE, Fact Sheet
of June 11, 1974). The hot non-contact cooling water discharged
to the River did not contain any chemicals; however, by fall 1978
all this water and the industrial waste water was routed to the
Lynden STP for treatment (Glynn, letter of January 14, 1980).
According to available information, Columbia Cement, Lynden Trans-
port, and Olivine have discharged industrial waste water into
their respective receiving waters since 1970 (Table II-2). Columbia
Cement utilizes a series of settling basins for all cooling, wash
and process waters. All waters from the settling basin that are
not reused are discharged to Bellingham Bay. Olivine Corporation
maintains a rock crushing and milling industry. A settling basin
has been utilized for waste water discharge since 1972 or earlier.
Turbidity is the only water quality parameter known to be affected
by this industry. Lynden Transport utilizes an oil separator to
remove oil and grease from truck wash water before it enters Fish
Trap Creek (Glynn,personal communication January 14, 1980).
In Table II-l ten facilities presently discharging processed
industrial or domestic waste to the ground (non-overflow lagoon,
septic tank/drainfieId, or spray irrigation) are shown. This does
-65-
-------
not constitute a direct discharge to receiving waters but ground
water may eventually contribute run-off to Bellingham Bay and its
tributaries. These ground discharge facilities will not be dis-
cussed in detail but do require consideration as potential contri-
butors to water quality degradation (coliform bacteria), DO, sus-
pended solids) of Bellingham Bay.
Municipal Facilities: Comparing the municipal facilities, the
Bellingham STP has contributed the highest average flow rate
(7.6 mgd (28. S mid)) over the past eight years (1972-1979).
The remaining facilities discharged .54 mgd (2.04 mid) and less.
In addition to sanitary sewage, this facility along with the
Lynden STP are the only municipal facilities to also receive
processed industrial waste for treatment and discharge (Table
II-5) .
The Bellingham STP began operations in 1947. Treatment consisted
of 2 primary clarifiers or qualified septic tanks, anaerobic
sludge digestion, sludge dewatering and an outfall discharging
at the end of "C" Street (CH2M Hill 1970} (Figure 11-11). In
1960 additional treatment facilities were installed to upgrade
treatment (additional clarifier,chlorination facilities, de-
gritting and sewage grinding facilities) and increased the plant's
capacity (CH2M Hill 1970). Treated waste was discharged through
the original "C" Street outfall. Untreated sewage from the south
end of Bellingham was released through an outfall located at Harris
and McKenzie Streets (Figure 11-11). There is no available infor-
mation to ihdicate if this outfall was active previous to 1960.
In June 1974 new primary treatment facilities were installed
and operative at Post Point (CH2M Hill 1974). Discharge of
untreated waste ceased, and all process waste was discharged
through a 2350 foot (716 meter) outfall off Post Point (Figure
11-12). This new primary system allowed for coagulation, centri-
fugation and incineration of sludge (DOE Fact Sheet of July 29,
1974).
-66-
-------
Table II-5 TREATMENT PROCESS UTILIZED BY MUNICIPAL AND DOMESTIC FACILITIES DISCHARGING TO BELLINGHAM BAY
Facility
Oper- Existing
ating Type of
Oats Type of Haste Treated Treatment
Existing Treatment Description of Treatment
Bellingham STP 1948
Processed industrial (
sanitary
Bellingham Hater
Treatment Plant
1974** Diverted Filter Backwash
Discharge to BeUingham
STP October 1978
Bverson STP 1974
Ferndale STP 1970
Lynden STP 1938
Lynden Mater 1924*
Treatment Plant
Sanitary
Sanitary
Processed industrial
and sanitary
Diverted Filter Back-
wash, Discharge to Lynden
STP in 1978
Primary Primary clarifier
c sludge incinera-
tion
N/A N/A
Secondary Oxidation Ditch
Primary/
Secondary
Secondary
N/A
Aerated Lagoon
Oxidation Ditch
Settling Basins
Primary clarifier removes settled floating solids allowing
for some reduction of organics. The effluent is chlorinated
previous to discharge» Sludge is incinerated using ashes as
soil conditioner.
The effluent is aerated and retained in the basin for
approximately 24 hra. Flows to clarifier for removal of
solids — then chlorinated previous to discharge. The wet
sludge is disposed" on land as soil conditioner.
Effluent is aerated in 1st basin t sent to a clarifier to
settle out solids. The effluent is chlorinated t discharged.
Sludge remains in the lagoon. A large buildup of sludge
necessitated removal t disposal in 1974.
Effluent is aerated by brushes which churn the wastewater.
The effluent is retained in the basin approximately 24 hra
and diverted to a clarifier to settle out solids (1-2 hrs
retention). Effluent is chlorinated and discharged. Sludge
dried in drying beds and used as nursery soil conditioner.
Hhatcom County
PUD «1
Hhatcom County
Infirmary
1966* Hater
1930's Sanitary
N/A
Primary/
Secondary
Clarifier
Trickling filter
Hater is puoped from the Nooksack River to a clarifier.
Aluminub sulfate and hydrated lime is mixed with the water
to remove solids and coloration. The settled sediment is
diverted to a holding pond to settle out solids. The
clear supernatant is returned to the Nooksack fUver.
Haste is screened £ clarified to remove settleable solids.
The effluent is passed through a standard rate trickling
filter to remove BOC 6 is then clarified a 2nd tima to re-
move solids. The effluent is chlorinated ( discharged.
Based on available permits and/or application on file at DOE, Northwest Regional office, Redmond, HA.
Initial operation of the facility may be earlier than Indicated.
I
Earliest data located in available reports. Initial operation of the facility may be earlier than indicated.
-------
1000 2000
4000
500 1500 3000 yards
Nookaack Rlv«r
Luramt
Indian
Reservation
Portage
Bay
Portals 1st
Point
Frances
Lummi W.
Bellingham
Bellingham STP
Outfall Idischarga
location!
POINT
Chuckanut
Bay
Bellingham
Bay
South Bellingham Outfall
I Discharge locations I
Ptoasant
Governors Bay
Point
Figure 11-11 DISCHARGE LOCATIONS FROM BELLINGHAM STP AND
SOUTH BELLINGHAM
Source: CH2M Hill 1970
-68-
-------
0 1000 2000
4000
500 1500 3000 yards
NoQkaack fflyar
Lummt
Indian
Reservation
Point
Frances
Lianml ftl.
Bellingham
Bay
Portage
Bellingliam
Post Point
Treatment
Plant
Outfall-
Pipe
* f
Chuckanut
Bay
piMMnt
Governors f\
Point
Figure 11-12 POST POINT TREATMENT PLANT AND OUTFALL LOCATION
Source: CH2M Hill 1974
-69-
-------
A high percentage of dissolved organic material occurs in processed
waste waters from food processing facilities (CH2M Hill 1976).
Only small concentrations of this material are removed by primary
treatment; therefore, increased BOD loads in the Bellingham STP's
effluent is expected. This will not be alleviated until secondary
treatment facilities are installed.
The Lynden STP initiated a trickling filter system in 1338, This
system was upgraded to an oxidation ditch in early 1979 (Sylvester,
.personal communication of January 8, 1980). Two industries
(Shuksan Foods, Seabrook Farms) diverted processed industrial
wastes to the plant after installation of the upgraded system
(Figure II-2).
Three water treatment plants (WTP) extract water from the Nooksack
(Lynden and Whatcom PUD #1 WTPs) or Whatcom Lake (Bellingham WTP)
i
for industrial and public use; however, only one (Whatcom PUD #11
WTP) discharges water (uncontaminated) back to the Nooksack River.
Previous to 1977 the Whatcom County PUD #1 WTP returned filter
backwash from the screening operations to the Nooksack River.
Installation of a settling basin alleviated this problem allowing
only the supernatant (water above the settled solids) to be returned
to the Nooksack. The Bellingham and Lynden STP facilities dis-
charged filter backwash to receiving waters until 1978 when all
waste discharge was diverted to the Bellingham STP and Lynden STP,
respectively.
The remaining three municipal facilities appear in Table II-5.
Available information indicates that each of their existing, types
of treatment facilities were in existence when plant operations
begem. These are explained in the referenced table.
-70-
-------
B. MILL CLOSURES
An evaluation of Georgia-Pacific mill closures is provided in the
following discussion. This quantitative overview allows for a
more complete analysis of the water quality and receiving water
bioassay studies evaluated in later chapters.
Available information (Georgia-Pacific Daily Monitoring Reports
(OMR)) from September 1968 to December 1974 provides a daily
average per month for each separate day; however, subsequent DMR's
only provide the daily averages for the entire month. The early
monitoring reports (September 1968 - December 1974) designate
routine closures for July 4th, Labor Day, and Christmas (December
24"—25) (Table II-6) . During these closures there is no production
of pulp, paper, paperboard or tissue; however, some pipes continue
to discharge a waste flow. The DMR's indicate that these main-
tained pipes are void of effluent constituents (BOD, SCS, TS, etfc.
whenever production is not operative. It is presumed that these
routine closures have continued to the present, but there is no
available information to verify these temporary shutdowns (Dec-
ember 1974 - present).
Mill production ceased on two documented occasions, June 23-25, 1970
and May 18-21, 1973 (Table II-6) (DMR June 1970, DMR May 1973).
There is no available correspondence to indicate a reason for these
closures. An extended Labor Day shutdown of the mill occurred
from midnight September 5, 1976 until the evening of September 8,
1976 (Table II-6) (Mowry, letter of August 18, 1976). During the
maintenance closure (September 7-8, 1976) the primary clarifier
was drained and inspected (Mowry, letter of August 18, 1976).
Available information indicates two strikes have occurred at the
Georgia-Pacific mill (Table II-6). For approximately 2 weeks in
autumn of 1964, a labor strike was conducted by workers at all
Puget Sound pulp mills (Woelke 1972). During this period, Georgia-
Pacific was shutdown from November 12-25, 1964 (Woelke 1972).
-71-
-------
Table II-6 SUMMARY OF DOCUMENTED MILL CLOSURES AT GEORGIA-PACIFIC MILL, BELLINGHAM, WASHINGTON
1964 - 1979
Routine Closures*
Closures*
Strikes
July 4
Labor Day 1968-1974
December 24-25
June 23-25 1970
May 18-21 1973
September 7^8 1976
November 12-25, 1964
mid-July 1978 - February
1979
*No available average per day for each month provided in DMR's subsequent to December 1974
i
-j
to
i
-------
The most recent major Georgia-Pacific strike began in mid-July
1978 and continued for roughly 6 months (February 1979) (Johnson,
personal communication of January 9, 1980, and DMR's July 1978 -
February 1979). During this time the only operational mill facili-
ties included the bleached sulfite pulpmill, tissue pulpmill and
alcohol plant which were maintained at a reduced level (Johnson,
personal communication of January 9, 1980). Permachem and paper
process pulps were not produced at this time.
The daily averages per month (OMR) required to be monitored for
Georgia-Pacific's effluent parameters (BOD, SCS, SSL, etc.) are
obtained from the total operative days during a calendar month.
Closures and strikes would not decrease daily averages unless the
mill maintained a reduced production. Biological oxygen demand
(BOD) was the only water quality parameter monitored extensively (
before, during and after the 6 month strike. Despite the fact tji^t
pulp production and waste flow were reduced by approximately 100*
average dry tons (adt) per day (90,700 kg/day) and 8.0 mgd/
day (30.3 mid) respectively, there was no significant reduction
in BOD. This may indicate that the decreased pulp production was
not significant enough to reduce the organic material in the
discharged effluent.
C. EFFLUENT-COMPOSITION AND TOXICITY
Georgia-Pacific Corporation in Bellingham is authorized to dis-
charge effluents through Outfall 9 into Whatcom Waterway, Bell-
ingham Bay in accordance with the conditions stated in the NPDES
Permit No. WA-000109-1 issued June 1, 1979. This permit applies
to both the sulfite pulpmill and the chlor/alkali plant. The
sulfite pulpmill is required to monitor the following parameters
on a daily or continuous cycle:
Production, tons/day for:
sulfite pulp
permachem pulp
waste paper pulp
Temperature (°F)
-73-
BOD
TSS
PH
Flow (mdg)
-------
The parameters that require daily or continuous monitoring by
the chlor/alkali plant include:
Total mercury TSS
Residual chlorine Flow (mgd)
pH
All sampling and analytical methods used by Georgia-Pacific are
reported to conform to the latest editions of the following references:
1. American Public Health Association, Standard Methods
for the Examination of Water and Wastewater.
2. American Society for Testing and Materials, A.S.T.M.
Standards, Part 23: "Water Atmosphere Analysis"""!
3. U.S. Environmental Protection Agency, Water Quality
Office Analytical Control Lab, Methods for Chemical
Analysis of Water and Wastes.
When one ton of wood is pulped by the sulfite process, approximately
half a ton of cellulose pulp is obtained. The other half ton of
original wood, along with the chemicals and water used for cooking,
or digestion, constitute the by-products of pulp milling collec-
tively known as sulfite waste liquor (SWL) or spent sulfite liquor
(SSL) (Gunter and McKee 1960).
Various classifications of potential toxicants are contained in
bleached sulfite pulp and paper mills. These toxic substances
can be divided into organic and inorganic compounds.
Organic Compounds
Fatty acids (FA)
Polar acids (PA)
Resin acids (RA)
Phenols (P)
Terpenes (T)
Juvabiones (J)
Chlorolignins
Inorganic Compounds
Heavy metals
Metals
Chemical additives
Within these two categories the literature permits some division
into major and minor toxicants. Many compounds, however, have
not been measured as to specific concentrations and effects. The
most important well-known (or suspected) toxicants of bleached
-74-
-------
sulfite pulp and paper mills in general are presented in Table .
11-7. The chemical constituents listed in Table 11-8 are chemicals
specific to Georgia-Pacific's effluent waters from both their
pulpmill and chlor/alkali plant. Table II-9 lists the quantities
of mercury and chlorine discharged by Georgia-Pacific into Whatcom
Waterway in 1973-1979. Chemicals discharged by other Pacific
Northwest sulfite mills are presented in Table 11-10.
Knowledge concerning the toxic constituents of SSL stems primarily
from the work of Wilson and Chappel (1973) who identified consti-
tuents corresponding to about half of the total toxicity in a
sample of the discharge from a high yield soda-base sulfite mill.
Resin acids represented about 26% of the total toxicity and roughly
half of the identified constituents. The two phenolic type
compounds, eugenol and trans-isoeugenol, represented about 20%
of the total toxicity and were responsible for the darkening of
fish integuments, which is a characteristic response of sulfite :
wastes. Another phenolic type compound responsible for about 8%£
of the total toxicity was 3,3' dimethoxy, 4,4' dihydroxystilbene.
BC Research {1976) states that the toxic components present in
calcium and magnesium base pulping mills are probably similar
overall to those identified in soda-base effluents.
-75-
-------
Table I1-7. KNOWN AND SUSPECTED TOXIC COMPOUNDS IN MILL
EFFLUENT FOR BLEACHED SULFITE PULPMILLS
MAJOR TOXICANTS : (Leach and Thakore 1977)
Abietic acid (RA)
Dehydroabietic acid (RA)
Isopimaric acid (HA)
Neoabietic acid (RA)
Palustric acid (RA)
Pimaric acid (RA)
SandaracOpimaric acid (RA)
Levopimaric acid (RA)
Chlorolignins
II. INTERMEDIATE TOXICANTS:(Walden 1976, Mueller et al. 1977)
Juvabione (J) &1' Dehydrojuvabione (J)
.1 •
Eugenol (P)*
Isoeugenol*
3,3* dimethoxy, 4,4' dihydroxystilbenei*
Dehydrojuvabiol
III. MINOR TOXICANTS; (Mueller et al. 1977}
Linoleic acid (FA)
Linolenic acid (FA)
Oleic acid (FA)
Palraitoleic acid (FA)
IV. COMPOUNDS OF UNKNOWN TOXICITY: (Rvasnicka and McLaughlin.
1955, Hemingway and Greaves 1973)
Acetaldehyde (PA)
Formic acid (PA)
Acetic Acid (PA)
Glycolic acid (PA)
Methyl glyoxal (RA)
Methyl.palustrate (RA)
Methanol (RA)
p - Cymene (T)
Acetone
Furfural
5 - methyl - furfural
Tetrahydrocadalane
2 - furoic acids
Furf ural alcohol
Manase
Xylose
Arabiriase
Vanillan
Vannillic acid
Conidendrin
Todomaturic acid
Mannonic acid
Gluconic acid
Arabonic acid
2 - conidendrin
Vanilloyl acetyl
Dehydroconferyl alcohol
* Toxicants that were classified in more than one of the toxicant
groups I - III were entered in this table in the most toxic
group where they were cited.
-76
-------
Table IIr-8 . CONSTITUENTS PRESENT IN THE EFFLUENT WATERS OF
GEORGIA PACIFIC'S PULPMILL AND CHLOR/ALKALI
PLANT. (NPDES Application 7/28/78) {Plant
Process and Discharge Description Oct 21, 1971)
Aluminium
Lead
Ammonia
Manganese
Antimony
Mercury
Barium
Molydenum
Beryllium
Nickel
Boron
Nitrate
Bromide
Oil and Grease
Cadmium
Organic Nitrogen
Chloride
Phenols
Chlorine
Phosphorus
Chlorinated Organic
Potassium
Compounds
Sodium
Chromium
Surfactants
Cobalt
Sulfate
Copper
Sulfide
Cyanide
Sulfite
Fluoride
Titanium
Iron
Zinc
Kjeldahl N.
-77-
-------
Table II-9 CONCENTRATIONS OF EFFLUENT CONSTITUENTS DISCHARGED
BY GEORGIA PACIFIC (Discharge monitoring reports,
Georgia Pacific).
Mercury 1978 average = 0.02 lbs/day (permit allows 0.07 lbs/day)
1979 average = 0.01 lbs/day (permit allows 0.07 lbs/day)
Residual Chlorine 197S average = 0.68 mg/1
1979 average » 0.55 mg/1
-78-
-------
TABLE 11-10 CONCENTRATIONS (p.p.m.) OF OTHER PACIFIC NORTHWEST PULP AND PAPER MILL CONSTITUENTS
SULFITE MILLS
1° Influent
1° Effluent
2° Effluent
Chemical
Range
X
Range
X
Range
X
References
FATTY ACIDS
1) Linolenic Acid
<0.02
<0.02
<0.02
Easty et al. 1978
2) Linoleic Acid
<0.02-0.12
0.07
<0.02-0.06
0.04
<0.02
•• II II II
3) Oleic Acid
0.04-0.20
0.12
0.02-0.14
0.08
0.02-0.12
0.07
II II M II
4) Epoxystearic Acid
<0.04
<0.04
<0.04
II II II II
5) Oichlorostearic Acid
<0.04
<0.04
<0.04
II II II II
PHENOLS
1) Trichloroguaiacol
<0.04
<0.04
<0.04
Easty et al. 1978
2) Tetrachloroguaiacol
<0.04
<0.04
<0.04
II II II II
RESIN ACIDS
I 1) Abietic Acid
-j
0.13-0.43
0.28
<0.02-0.10
0.06
<0.02
Easty et al. 1978
vo
l
67.4
Leach & Thakore 1977
2) Dehydroabietic Acid
51.8
Leach & Thakore 1977
2.06-2.92
2.48
1.00-1.72
1.36
<0.02
Easty et al. 1978
3) Isopimaric Aicd
r-
•
00
Leach & Thakore 1977
0.06-0.11
0.09
<0.02-0.08
0.05
<0.02
Easty'et al. 1978
4) Pimaric Acid
9.8
Leach & Thakore 1977
0.06-0.09
0.75
<0.02-0.03
0.02
<0.02
Easty et al. 1978
5) Dichlorodehydroabietic
Acid
<0.04
<0.04
<0.04
II II II II
6) Monochlorodehydro-
abietic Acid
<0.04-0.48
0.04
<0.04-0.48
0:Q4
-<0.04
II II II »
OTHER
1) Chloroform
0.006-0.023
0.145
0.057-0.127
0.092
0.007-0.011
0.009
II II II M
-------
REFERENCES
303e Staff. October 1975. 303(e) Water Quality Management Plan.
Water Resource Inventory Area 01, Nooksack Basin. Department
of Ecology, State of Washington.
American Public Health Association (APHA),- American Water Works
Association and Water Pollution Control Federation. 1976.
Standard Methods for the Examination of Water and Waste Water
14th Edition. APHA, Washington, D.C. 1 :
American Society for Testing and Materials. A.S.T.M. Standards,
Part 23: "Water Atmosphere Analysis".
B.C. Research. March 31, 1976. Identification of the Toxic
Materials in Sulphite Pulp Mill Effluents. CPAR Project
Report 407-1. Pulp and Paper Pollution Abatement. 56 pp.
Cameron, Bruce A. July 19, 1977. Order Docket No. DE 77-376
to K. Hertz, City of Bellingham.
Cameron, Bruce A. July 19, 1979. Personal communication to
Kathy Pazera, Biologist, Northwest Environmental Consultants,
Inc. (NEC).
CH2M Hill. 1970. Pollution Control for Bellingham Bay. Sewagei
Facilities Design Study. 110 pp + Appendix. 1
CH2M Hill. May 1974. Water Quality Management Plan* Phase I
Reports Whatcom County Washington (WRIA 01, 03, 04) prepared
for the Whatcom County Council of Governments, Bellingham, WA.
CH2M Hill. April 1976. Bellingham Bay Monitoring Program. A
Report on Receiving Water and Sediment Quality in the
Vicinity of the Post Point Diffuser Outfall, Bellingham,
Washington. Prepared for City of Bellingham and Georgia-
Pacific Corp. 63 pp.
Easty, D.B., L.G. Borchardt, B.A. Wabers. 1978. Removal of
Wood-derived Toxics from Pulping and Bleaching Wastes.
Environmental Protection Technology Series. EPA-600/2-
78-031.
Fiedler, Glen H. April 4, 1974. Letter to C.H. Thompson, Chair-
man, Hazardous and Toxic Substance Regulation Task Force.
Garner, John. February 6, 1980. Letter to Kathy Pazera, Biolo-
gist , NEC.
Gearherd, Jim. January 17, 1980. Personal communication to Kathy
Pazera, Biologist, NEC.
Gearherd, Jim. February 11, 1980. Personal communication to
Kathy Pazera, Biologist, NEC.
Georgia-Pacific Corporation. October 1972. Process Design Report.
Mercury Recovery from Sediments and Sludges. Part I: Sludge
Treatment Project 12040 HDU.
-80-
-------
Georgia-Pacific Corporation. Daily Monitoring Reports (DMR)
submitted to DOE. 1966 - 1979.
Glynn, John. January 14, 1980. Personal communication to Kathy
Pazera, Biologist, NEC.
Gunter, G. and J. McKee. 1960. On Oysters and Sulfite Waste
Liquor. Washington Pollution Control Commission. 93 pp.
Hemingway, M.W. and H. Greaves. 1973. Biodegradation of.Resin
Acid Sodium Salts." TAPPI, Vol. 56. No. 12. December 1973.
pp. 189-192.
Johnson, Bruce. January 22, 1979. Personal communication to
Kathy Pazera, Biologist, NEC.
Johnson, Bruce. January 9, 1980. Personal communication to
Kathy Pazera, Biologist, NEC.
Kvasnicka, E.A. and R.R. McLaughlin. 1955. "Identification of
Spruce Sulfite Liquor Components." Canadian Journal of
Chemistry 33:637.
Leach, J.M. and A.N. Thakore. 1977. Compounds Toxic to Fish
in PulP Mill Waste Streams. Prog. Water Tech. Vol. 9,
pp. 787-798. Pergamon Press.
Mowry, Warren. August 18, 1976. Letter to Bruce Johnson, Depart-
ment of Ecology.
Mueller, J.C., J.M. Leach and C.C. Walden. 1977. Detoxification
of Bleached Kraft Mill Effluents - A manageable problem.
TAPPI Environmental Conference April 25-27, 1977. pp. 77-80.
Permit Application. July 28, 1978. Application for NPDES permit
to discharge wastewater. Form C. Applicant was Georgia-
Pacific.
Peck, Larry. February 7, 1980. Personal communication to Kathy
Pazera, Biologist, NEC.
Permit Application. July 28, 1978. Application for NPDES permit
to discharge wastewater. Form C. Applicant was Georgia-
Pacific.
Permit No. WA-000109-1. NPDES Permit issued by Washington Depart-
ment of Ecology (DOE) for pulpmill discharge. Issued
May 13, 1975; re-issued June 1, 1979 to Georgia-Pacific.
Permit No. 2900. February 23, 1968. Permit issued to Oesar
Cedar Company.
Permit No. T-2862. May 27, 1968. Waste Discharge Permit issued
to Georgia-Pacific by the WPCC.
Permit No. T-3456. March 16, 1973. NPDES Permit issued by the
Washington Department of Ecology to Georgia-Pacific.
-81-
-------
Sylvester, Bob. January 8, 1980. Personal communication to
Ka-thy Pazera, Biologist, NEC.
.U.S. Environmental Protection Agency, Water Quality Office
Analytical Control Lab. Methods for Chemical Analysis of
Water and Wastes. 1974. EPA-625/6-74-003. EPA, Washington,D.c.
Walden, C.C. 1976. Review Paper: The Toxicity of Pulp and Paper
Mill Effluents and Corresponding Measurement Procedures.
Water Research, Vol. 10, pp. 639-664. Pergamon "Press. 1976.
Washington State Department of Ecology. June 11, 1974. Fact
Sheet and Technical Information,Consolidated Dairy - Darigold.
Washington State Department of Ecology. July 29, 1974. Fact
Sheet and Technical Information, Consolidated Dairy -
Darigold.
Washington State Department of Ecology. January 1978. Chapter
173-201 WAC Water Quality Standards for 'Water's of the State
of Washington. 11 pp.
Wilson, M.A. and C.I. Chappel. 1973. Reduction of Toxicity of ¦
Sulfite Effluents. CPAR Report No. 49-2. Canadian Forestry
Service, Ottawa,Ontario.
Woelke, C.E. October 1972. Development of a Receiving Water
Quality Bioassay Criterion Based on the 48 Hr Pacific Oyster
' ~ * Mngton Department of
93 p
-82-
-------
III. OCEANOGRAPHIC DYNAMICS
This chapter describes the dynamics of Bellingham Bay and adja-
cent waters as documented by research during the last three
decades. The data is generally somewhat fragmentary, and as-
sumptions and data standardization are often necessary to pre-
sent a clear and complete picture of current patterns, efflu-
ent dilution and other important processes. Methodologies are
presented below upon which analysis of these parameters is
made in later chapters (see Chapter VIII). Due to the large-
scale influence of currents, the study area for oceanographic
dynamics is considered to include Rosario Strait and its ap-
pended bays (see Figures III-l and III-2) including Bellingham,
Samish, Padilla and Fidalgo Bays (referred to in this chapter
as the Rosario Appendage (RA)).
Major industrial facilities in RA have included two pulp mills that
now discharge through offshore diffusers. Effluent from the
Georgia-Pacific Corporation mill (hereafter GP) is presently
discharged into Bellingham Bay (Figure III-2); effluent from
the Scott Paper Company mill (hereafter SP) was discharged
into Fidalgo Bay and Guemes Channel. The mill discontinued
operation in March 1978.
The interaction of pulp mill effluent with the biological and
chemical processes is undoubtedly complex. Reported here is a
synthesis of physical aspects of circulation that bear on the
dispersion of material inputs concentrated primarily in the
surface layer in RA and its approaches.
The behavior of pulp mill effluent is variable in time and
space. Selected aspects of the dispersion of effluent have
been described for Puget Sound and approaches by Bartsch et al.
(1967); from the GP mill by Collias et al. (1966); and for the
SP mill at Anacortes by the Washington State Water Pollution Control
Commission (1967). These and other reports are summarized
-------
* f
rafeteaxtesa
. . . * -*«» 4K.^V A
•->•? ^ 1»
w^-*^*. /g^, %. < cv t; *•
*,. ^^g^WieTJomA
^V STUDY. +»
*.'
^X y
Fuci
<~4.« «*s~ * i-"-6--»
J , T?-^v?$V * -" \ ^ ^
r-i^h-r -*?
' Jj^ "* 4tStS^ 4
.^'Tf
i^r
• ¥ »f1
Tr -*-
Pacific
Ocean
__ ' -:&.1
*~#» * *< Jft"**** *+?
,v --HHM-4J8. .« . - ,-v "t^1Sl
S^. -.. ; v --v"kz^x***
»* ~ Tsi ^iiMUrf^ * ** *
«£„ * At >y» f «*•*? *S8fe
&1T...I
' j
*Vx^
¦
\~ < 3t;£fet r
*
V%4?~
'w mcc
V a4^^,t -<>$>„ ~ '
?s^^;» - «*.
v« &jgK
i"? i* v« ft" '- «•«
.%**>, •V'VV,-
*** "" 'JC*
- »»"¦:,, *4
*x» v-V#l
, & ^ -TS" » - '!
«WShwIsmMHw>wbw
V'^^, . Js, '
Figure III-l OVERVIEW OP OCEANOGRAPHIC STUDY AREA
key:
>huh- Major Sills
-34-
-------
Strait of
Georgia
Lumml Bay | /^ommk
feMMM
idMim
mmm
Baittngham
Portage BayAPortafle *
IsL O
-® Pt,
\
Chucfcanut Bay
Pleaeant Bay
mm*
Utftnrt:
iNSWfc;
Carter
Pt.
San Juan
Islands
Clark
Samtah Bay
Guamaa. Channel
FMalgo
Bey
Padllla Bay
100 200
50 150 300
thousands of feet
Figure III-2 0CEAN0GRAPHIC STUDY AREA
-85-
-------
below in order to obtain patterns of circulation and describe
the effluent pathways and dilution using existing data of
water properties and currents.
The following sections of this chapter describe the .per-
tinent physical aspects of the study area, sources of field
data, mean and fluctuating currents, characteristic time scales
of water movement, and dispersion and dilution of material
inputs.
A. PHYSICAL AND GEOGRAPHIC CHARACTERISTICS
The study area encompasses a complex of interconnected bays
which exchange water with Rosario Strait through a matrix of
channels and passages (Figure III-3). Table III-l lists the
sill depths for the various channels and passages. These sills
are important in moderating the exchange of deep water between
RA and Rosario Strait. A shallow sill occurs between Lummi
Island and Lummi Bay (~5 m depth (at mean lower low water))
and restricts the exchange of water through Hale Passage. The
shallowest sill occurs between Portage Island and Lummi Penin-
sula ("0 m depth (at mean lower low water)); however there is
limited exchange of water between Bellingham Bay and Hale
Passage at certain high tides. Between Cypress and Sinclair
Islands there is a sill having approximately 40 m depth.
The sill depth in Guemes Channel is 13 m. The deepest access
for water from Rosario Strait occurs just south of Lummi
Island and is directed into the mouth of Bellingham Bay along
the eastern side of Eliza Island.
An exchange of water can occur between the four bays because
of the common access to Rosario Strait in the area near Vendovi
Island. In particular Bellingham Bay and Samish Bays are con-
nected at their mouths.
The majority of material inputs into RA enter Bellingham Bay
-86-
-------
N
.thousands of
¦*«•*/»«•>. ; • •
3
I
»••••
3
£?•••
vM'w.V;.- . • •
Figure III-3 BOTTOM CONTOURS IN THE ROSARIO APPENDAGE
(Fathoms)
See Table III-l for sills
-87-
-------
Table III-l. SILL DEPTHS WITHIN THE STUDY AREA
Depth at MLLW (m)
Sill
Deepest
Mean*
1.'
Green Point - Victoria
115
60
2.
Pt. Partridge -Smith Is. -Iceberg Pt.
70
36
3.
Guemes Is. - Reef Pt. (Cypress Is.)
44
23
4.
Ahacortes — Guemes Is.
13
9
5.
Cypress Is. - Orcas Is.
56
45
6.
Cypress Is. - Sinclair Is.
39
18
7.
Sinclair Is. - Jack Is. - Guemes Is.
39
17.5
8.
Sinclair Is. - Lummi Is.
67
42
9.
Lummi Pt. - Lummi Penninsula
5
4
10.
Eliza Is. - Portage Is.
10
5
11.
Portage Is. - Lummi Peninsula
0
0
*
Mean sill depth is defined as the cross sectional area divided
by the cross section length at mean lower low water.
-------
at its head. The major direct inputs of freshwater are from
the Nooksack River, which enters the northern end of Bellingham
Bay, and the Samish River which enters the southern end of Samish
Bay. Freshwater input to the Strait of Georgia and the Strait
of Juan de Fuca can enter through the mouth of the RA. The
major inputs of mill effluent occur at the.eastern edge of
Bellingham Bay near its head and the western boundary of
Padilla Bay near its mouth. The source of water near bottom
is from the Strait of Georgia via northern Rosario Strait and
the channel between Sinclair and Lummi. Islands.
The characteristic dimensions of the component Bays have been
summarized in Table III-2, based on recent bathymetric charts
(see Figure III-4 for boundaries). The total surface area of
RA is about 318 km2, or about 5% of the surface area of the
Strait of Georgia; and 12% of the surface area of Puget Sound.
B. DATA SOURCES AND METHODS
Data presented in this section were obtained from municipal,
state, federal, and private institutions. Materials reviewed
contained data on the tides, currents, winds, water properties,
runoff, and sedimentation of RA and its approaches. In addi-
tion mercury and pulp mill effluent were used as tracers of
the movement of man-made inputs. Sources of the data are as
follows:
1. Tides
The National Ocean Survey (NOS 1980) tide tables list predictions
of tides at the municipalities of Bellingham and Anacortes
(Figure III-2). In addition Parker (1977) reported results
for numerous tide stations throughout the San Juan Islands
and RA. The mean range is defined as the difference in height
between mean high water and mean low water. The spring range
is the average s^mi-diurnal range occurring semimonthly in
association with a new or full moon. The diurnal range is
-89-
-------
Table III-2. CHARACTERISTIC DIMENSIONS AND RATIOS OF ROSARIO
APPENDAGE3
Ball. Saalah Padllla fUdgo Ball.*Saaiah fadllla>Fldalgo Vhol*
Bay . Bay Bay Bay Syataa Syacaa Syataa Dnlt»
1) taBfCh, astraaea
' to haad
8.64
7.62
11:9
3.7
23.9e
18.5*
37.0*
ka
2) Croat aactlaaai *tm
at aatxaaea
17.2
14.9
26.0
0.8
37.4
18.5
34.1
104.1
3) Surface ana at KLU)
54.2
38.7
30.56
4.89
178.59
74.72
253.31
106
4) Surface area at MB)
70.32
52.43
60.39
7.78
209.47
108.35
317^82
10* a2
-S) Maan tlda hatgbc
1.39
1.39
1.52
1.32
1.59
1.52
1.36
«
6) Voltna balov MUM
780.3
266.19
118.90
8.37
468B.38
837.92
3526.30
10® a3
7) Voluaa batman HUH
b MB)
166.12
63.54
69.11
9.63
589.80
139.12
728.92
106 a3
kUu
8) Mun dapeh • Voloat(t)/
aucfaca acaa(3)
14.40
6.88
3.89
1.71
26.23
11.21
21.82
a
9) Bulk raatdaaca pazled *
Voluaa(6)/tU*l pfiaa(7>
4.69
4.19
1.72
0.87
7.95
6.02
7.58
Ildal
Cyclaa
10) Haas tidal nana pert •
tidal pri«a(7)/
% cldal day
.744
.284
.309
.043
2.638
.622
3.261
* 10* a* i
11) Ghataetartacle tidal
apaad « tidal prl*n<7)/
exoaa aactlaaai ataa<2)/
% tidal day
.043
.019'
.012
.034
.071
.034'
.096
a a"1
12) KB • CDaffaatarlatle
tidal apaaddl*)
.00183
.00036
.00016
.00292
.00504
.00116
.00922
a2.'*
Veotaetaa on T*bl« 2 > Maaaalcu and btloa of totarlo Appasdaga.
a. Roaario Appaadata ilvlttcu dam ta Flgora III"4.
b. Scaa values and azaa* tttm Celliaa at al. (ISM).
e. Haad of Balllacbaa Bay to haad ta Saalah Bay.
d. Vaadovi Ialasd ta haad of Fad 11 la Bay.
a. Haad ot SallinjbaB Bay to baad of Fadllla Bay.
-2 a-
-------
Strait of
Georgia
T
NMtamkvMllH:::
Lummi Bay
t / Lmtanl
ftMSUM
va/UonJ
Portage Bay7\Porta«e
• c-rrv 7\isi.
fillip
Eliza
1st.
San Juan
Islands
Sinclair
Isl.
Clark
Cypres*
tVandovi
Isl
William" ,
0 Pt. ~i
f
2 p-y
CO P»f
>
<
a
Chuekanut Bay\
* Pteasant Bay
i
<
<0
1
2
*
O
*
Sattngham
-• • f
if
Samish Bay
Samish
Isl.
8
i
s
ui
t-
= §2
0>
Fidalgo
Bay
Arocortes*
i
<
s *
2"
100 200
400
Padilla Bay
50 150 300
thousands of feet
Figure III-4. BOUNDARIES OF BELLINGHAM, SAMISH, FIDALGO, AND
PADILLA BAY SYSTEMS
-91-
-------
the difference in height between mean higher-high-water and
mean lower-low-water. The mean and diurnal ranges for Belling-
ham are 1.6 m and 2.6 m, respectively; the mean and diurnal
ranges for Anacortes are 1.5 m and 2.5 n, respectively.
2. Currents
Currents have been measured using current meters at several
locations within RA and approaches. Summaries of these obser-
vations are listed in Appendix A. The majority of measure-
ments within Bellingham Bay were taken by Collias (.1971)
during April and May 1963. The measurements were obtained
using Richardson current meters moored with surface buoys.
The observations consisted of current speed and direction
(one minute averages recorded every 10 minutes) at approxi-
mately 3 and 20 m depths. Twelve moorings were deployed for
each of two periods (23 and 19 days) beginning on 17 April and
7 May 1963. Of the 22 current meters deployed, 16 appeared to
function properly where both speed and direction were obtained;
for six current meters only speed was obtained.
Other measurements have been taken by the U.S. Geological
Survey (US6S) and NOS. These records were obtained from
NOS and NOAA. Some of these data were previously reported
by the Washington State Pollution Control Commission (1967),
Schumacher and Reynolds (1975), NOS(1976), Parker (1977), and
the Tidal Current Table (NOS 1980). Current meter results are
shown and analyzed in Chapter VIII.
Currents have also been measured by tracking the movements of
several drifting materials: dye, drogues* and drift sticks.
These observations are summarized in Appendix A. Within Belling-
ham Bay Collias et al. (1966) and Driggers (1964) reported
the movement of rhodamine B dye initially released offshore
-92-
-------
drogues, drift sticks, and drift poles in the area between
Bellingham and Samish Bays. The Army Corps (1977) also tracked
drogues over a possible dredge disposal site located near
Eliza Island.
Within Padilla Bay and Guemes Channel studies were conducted
by the Washington State Water Pollution Control Commission
(Wagner et al. 1957).
Within the, inner Strait of Juan de Fuca 5000 drift cards were
released by Pashinski and Charnell (1979). Some of the cards
entered Rosario Strait and the Strait of Georgia.
3. Winds
The patterns of prevailing winds over the Strait of Juan de
Fuca and Puget Sound have been diagrammed by Harris and Rattray
(1954) (Figure III-5). Winds have been computed in the area
by Overland et al. (1978) using numerical models; their results
are as yet unpublished, but some wind patterns have been pre-
sented by Cannon (1978). Mean hourly wind speed and direction
have been presented for the period 1950 - 1954 at Bellingham
Airport by Collias et al. (1966). Winds were also measured
over the water by the Washington State Department of Fisher-
ies (1957 - 1959) (Westley 1957, Westley and Tarr 1959, 1960)
and Collias and Barnes (1962) as they collected water samples.
The study area is unique in that throughout the year the winds
are typically from the south. The five year record of hourly
winds taken at Bellingham airport shows that the mean hourly
wind speed was directed from south to southeast in all months
(Figure III-6). Highest mean speeds occurred November through
January and were directed from the southeast.
-93-
-------
OCTOBER-MARCH
APRIL - MAY
i
JUNE - OCTOBER
f Figure III-5 SEASONAL PROGRESSION OF PREVAILING WINDS
I (Adapted from Harris and Rattray 1954)
I Note: Arrows not to scale.
-------
18
16-
14-
±> I2i
UJ
<
K
UJ
a. _j
2 8
u .
H
tt 6"
<
t-
—AHACORTES
j'f'm'a'm'j'j'a's'o'n'd'j
I I
(»•')
WIND SPEED (msH) and DIRECTION ("T)
SAMISH R.
Figure III-6 ANNUAL VARIATION OP AIR TEMPERATURE, WIND, RIVER RUNOFF
AND PRECIPITATION.
Source: Collias et al. 1966, USGS Water Supply Papers
1971, 19 7T,"University of Washington 1953
-95-
-------
Although the distribution of wind stress with depth in the
study area has not been determined it is well known that wind
effects are often most pronounced near the water surface.
Collias et al. (1966) has presented surface patterns of tem-
perature, salinity, and SSL. Their observations also included
wind speed and direction at each hydrographic station (Collias
and Barnes 1962).
4. Runoff
Monthly average river discharges were obtained for the Nooksack
River (1951 - 1979), Samish River (1961 - 1970), Frazier River
(1931 - 1970), and Skagit River (1931 - 1970) from the U.S.
Geological Survey (Figure III-6). Monthly average discharge
from 1958 - 1962 has been presented by Collias et al. (1966)
for the Nooksack and Samish Rivers, and Fishtrap Creek (Fish-
trap Creek is included in the Nooksack River runoff 10 year
mean). The minor discharges of selected creeks entering RA
have been tabulated by Webber (1975, 1977). Collias et al.(1966)
has tabulated the gauged and ungauged drainage basins feeding
the above rivers and creeks. Finally the transport of water
through Swinomish Slough has been summarized by McKinley et al.
(1959). Elsewhere the total runoff data for the Strait of
Georgia (1950) were that of Waldichuk (1957) and the data for
Puget Sound were determined from monthly average discharge data
(1951 - 1970) using Lincoln's (1977) technique.
5. Water Properties
Within RA water properties were sampled from 1956 - 1959 by
the Washington State Department of Fisheries (Westley 1957,
Westley and Tarr 1959, and Westley and Tarr 1960); 1959 -
1961 by the University of Washington (Collias and Barnes
1962); 1962 - 1964 by the Washington State Water Pollution
Control Commission (1967); and 1972 - 1975 by Hill (1976).
Other less extensive surveys were conducted at less regular
intervals. The various observations are summarized in Appendix
B and in Chapter IV.
-96
-------
In the approaches to RA water properties have been sampled
by U.S. and Canadian institutions. Collias (1970) tabu-
lated stations in Rosario Strait and the Strait of Juan de
Fuca: temperature, salinity, and dissolved oxygen have been
sampled at selected mid-channel locations since 1932. Observa-
tions by Canadian institutions include those of Waldichuk
(1957), Redfield (1950) , and Crean and Ages (1971).
6,. Air Temperature and Precipitation
Figure III-6 shows the monthly average rainfall (1910 - 1940)
and air temperatures at Bellingham and Anacortes (Bellingham,
"18 years; Anacortes, "25 years; years unknown tabulated by
the University of Washington (1953). Tabulations of monthly
rainfall and precipitation for 1953 - 1963 were presented by
Collias et al. (1966).
7. Sedimentation
The Fraser, Nooksack, and Skagit rivers all carry significant
loads of suspended sediments at times. Within RA sediments
originating from the Nooksack and Samish rivers have been
examined and charted by Sternberg (1961). Sediment plumes
from the Fraser and Skagit rivers have been observed using
satellite photography by Feely and Lamb (1979) and from water
samples by Baker et al. (1978).
8. Pulp Mill Effluent
Effluent discharge data were obtained for both the GP and SP mills,
although only Georgia-Pacific presently remains in operation.
Discharge data for three selected periods prior to 1966 have
been reported for both mills by the U.S. Environmental Protection
Agency (EPA) and summarized by the Washington State Water Pollu-
tion Control Commission (1967). Monthly average discharge data
from 1966 - 1978 for Georgia-Pacific were obtained from the Wash-
ington State Department of Ecology (formerly the Washington
State Water Pollution Control Commission) and the EPA. Average
discharge data for the SP mill were obtained from Bruce Johnson
of the Washington State Department of Ecology (personal communi-
cation) . (See also Chapter II.)
-97-
-------
9. Mercury
GP operates its own Alkali plant on its Bellingham property.
From 1965 to 1970 effluent from this plant contained compara-
tively high levels of mercury. After discharge into Bellingham
Bay some of the mercury enters the bottom sediments. The dis-
tribution and concentration of mercury in the bottom sediments
has been discussed by Nelson (1974).
10. Aerial Photographs
Aerial photographs of the study area have been taken by several
sources as listed in Appendix C. Both satellite and low
altitude photos were examined for patterns of suspended sedi-
ment and Georgia-Pacific effluent.
11. Oil Spill
In 1971 approximately 880 m3 (230,000 gallons) of Number 2
diesel oil was spilled at the Texaco refinery near Anacortes,
Washington. A description of the spilled oil's movement on
the water surface has been presented by Vagners and Mar (1972).
In addition some oil was detected in water drawn from depth
inland of Deception Pass in Puget Sound by personnel from the
University of Washington. Description of the oil movement was
obtained from Professor Clifford A. Barnes (personal letter
to the Washington State Department of Ecology dated 26 Novem-
ber 1974) as reported by Ebbesmeyer et al. (1980).
C. FLOW CHARACTERISTICS
Currents that affect effluent dispersion may be divided into
mean and fluctuating components. Patterns of the mean current
suggest pathways of effluent movement over large areas. The
fluctuating current tends to disperse the effluent.
The current components have contributions from several mechan-
isms including thos« associated with tides, winds, runoff, and
-98-
-------
the intrusion of oceanic waters at depth. Although it is
difficult to assess the relative contributions of the various
mechanisms it is useful to quantify their overall effects as
summed in the two components. The mean is characterized by
its speed and direction an4 the fluctuations are characterized
by variance about the mean which is proportional to kinetic
energy.
1. Mean Currents
The vertical section at mid-channel of mean flow from the Strait
of Juan de Fuca into the Strait of Georgia has been discussed
by Waldichuk (1957) following Redfield (1950), and into Puget
Sound by Barnes and Ebbesmeyer (1978). These earlier studies
indicated that the flow into the Strait of Georgia and Puget
Sound consists o£ surface freshwater flowing seaward and bottom
water moving landward through Admiralty Inlet and all the San
Juan Island Passages of sufficient depth (Figure III-7). Deep
water flowing landward is mixed with seaward flowing surface
water over a series of sills. The reversal of flow occurs at
different depths in the various passages. In Puget Sound and
the Strait of Juan de Fuca these depths appear to be approxi-
mately 50 m and approximately 80 - 100 m, respectively.
The pathway of water from the ocean near the bottom has been
demonstrated by Barnes et al. (1972) using seabed drifters
(Figure III-8). They released seabed drifters off the Oregon
and Washington coast and recorded a significant number of
recoveries onshore. There were several recoveries in the
Strait of Juan de Fuca, Strait of Georgia, and Rosario Strait.
In general the pattern supports net landward flow near the
bottom.
Recent current meter measurements taken by the NOS (1976) indicate
that for the Strait of Georgia only Haro Strait has a typical
landward movement of bottom water; Rosario Strait has a net
seaward movement of water at all depths (Figure III-9). The
-------
JUAN OE FUCA CANYON
STRAIT OF JUAN DE FUCA
SAN JUAN PASSAGES
STRAIT OF GEORGIA
I
H*
O
O
I
I I I
-100
200 PUGET SOUND 300
* ' ' '
ItI 600
B
•. "t. s.
I I I
o
OCEAN
ENTRANCE
i i
100
200
i i
300
DISTANCE INLANO (km)
Figure III-7. CROSS SECTIONAL VIEWS OF THE PUGET SOUND - STRAIT OF JUAN DE FUCA - STRAIT
OF GEORGIA SYSTEM
Source: Adapted from Ebbesmeyer and Barnes 1980 & Waldichuk 1957.
Lower panel: Bottom profiles from mid-channel to head'of Port Angeles Harbor, Port Townsend
Bay, Bellingham Bay & Everett Harbor
-------
w —
•6s-
<\ AV Y2
VANCOUVER
ISLAND
JUAN OS FUCa
I
*> Rhwr mouttl
<40 m
> 40 m
X No
Figure III-8 PATHWAY OF SEABED DRIFTERS RELEASED
OFF THE WASHINGTON AND OREGON COASTS.
Source: Barnes et al. 1972
-101-
-------
HARO
STRAIT
ROSARIO
STRAIT
ENTRANCE
CHANNELS
BELLINGHAM
BAY
80 -
40
60
^ 80
£
mo-
il.
u
o
120
MO
160
180
• Vh*
• -4
"¦a
'3 (2)
r
20b
20o
1
• ^ *
NOS 47
(4)
*
200 i 1—-i 1—i 1 « 1 i—i r
60 40 20 O 20 40
EBB FLOOD
t
I
I
~
£>1103 Wb
"3:
<
-------
records indicate that landward flow through Haro Strait occurs
below 100 m. There is no net flow landward (northward) indi-
cated through Rosario Strait.
2. Vertical Exchange
The vertical structure of the mean flow patterns in RA have not
as yet been resolved. Collias (unpublished) measured the mean
currents at two depths (approximately 3 and 20 m depth), in
contrast Cannon (1973) used seven current meters to resolve the
vertical profile of mean currents in Whidbey Basin (see Barnes
and Ebbesmeyer 1978).
D. WATER PROPERTIES
The net movement of water may also be deduced in certain
instances from observations of water properties. The com-
position of Bay water is examined in the following sections,
and the effects of winds at surface are illustrated. These
factors serve as. input to the computation of bulk residence
times of freshwater and SSL in Chapter VIII.
1. Time and Space Variability
Figure 111-10 shows the average annual surface and bottom
water temperature, salinity, and dissolved oxygen from the
mouth of the Strait of Juan de Fuca through Haro and Rosario
Straits into the Strait of Georgia, and through Admiralty Inlet
into Puget Sound. The impact of tidal mixing over sills may
be illustrated by the landward changes in the water properties,
especially near bottom. The oceanic source water that traverses
the Outer Strait of Juan de Fuca shows comparatively small
changes in water properties whereas there are sharp increases
in the more energetic Inner Strait. In Haro and Rosario Straits
there are also sharp changes in the measured properties. How-
ever, bottom water in Rosario Strait is probably a mixture of
mid-depth and surface water from the Strait of Georgia.
-103-
-------
STRAIT OF JUAN DE FUCA
Of • 9
SAN JUAN PASSAGES
STRAIT OF GEORGIA
PU6ET SOUND
—
BOTTOM
/ Y
% /
10 * >*¦*¦*
*—<*• *r~
0
OCEAN
ENTRANCE
DO
ZOO 300
OISTANCE INLAND (km)
400
Figure 111-10 WATER CHARACTERISTICS OF PUGET SOUND AND ASSOCIATED
ESTUARIES Source: Evans-Hamilton, Inc. in house data
-104-
-------
The monthly progression of temperature (T) and salinity (S)"
versus depth may be shown conveniently on the T-S plane
(Appendix D ). Diagrams are presented for long term averages
of water properties in the Bay? off Entrance Island in the Strait
of Georgia based on data summarized by Pickard (1975) » an<* at
hydrographic station H2 in the Inner Strait of Juan de Fuca as
shown by Ebbesmeyer and Barnes (1980). These diagrams show
that water near bottom in the Bay resembles the character-
istics of water at 20 - 50 m depth in the Strait of Georgia.
Collias et al. (1966) concluded that water from Rosario Strait
flows along the bottom northward to the Bay.
Seasonal cycles of the measured variable are shown in Figure III-ll.
Temperature, salinity, dissolved oxygen and SSL were sampled at
approximately monthly intervals from 1956 to 1961 at a number of
stations throughout RA by the WDF (Westley 1957, Westley and Tarr
1959, 196.0) and Collias & Barnes (1962). Those stations taken within
Bellingham Bay (north of Francis Island - Post Point) were avea.
aged at selected depths (near surface and 20 m) in the Bay and
compared with stations in the Strait of Juan de Fuca (New Dungen-
ess NE) and the Strait of Georgia (Entrance Island). Values near
surface are averages of WDF and Collias data, whereas those at
20 m depth are only those of Collias due to lack of data at
depth in the WDF reports. Seasonally averaged vertical profiles
of the measured variables (Figure 111-12) are based only on
Collias data due to the limited depths sampled by the WDF. Ver-
tical profiles of water properties are also provided for months
of high and low local runoff (Figure 111-13).
E. EFFLUENT DILUTION
For an initial perspective it is useful to compare the volume of
effluent discharged during a year by the GP and SP mills with
the volume of water in the Bellingham-Samish Bay system and the
Padilla-Fidalgo Bay system, respectively. Both mills are considered
to determine any possible effect upon the background level of pulp
mill effluent present in RA contributed by the Scott Paper mill.
-105-
-------
o
V.
5
IE
Ul
K
20m
8
12
SURRtCC
20
24
20
32
28
32
8
%*
I
20
>
K
175
z
ui
Q
22-
M 0
0.8
0
1
I
Z
g
3
20a
0.4-
NTH
Figure III-ll SEASONAL CYCLES OF TEMPERATURE, SALINITY, DENSITY, AND
DISSOLVED OXYGEN IN BELLINGHAM BAY (Solid), OFF ENTRANCE
ISLAND IN THE STRAIT OF GEORGIA (dash-dot), AND AT NEW
DUNGENESS NE IN THE STRAIT OF JUAN DE FUCA (dashed).
Sources: Collias and Barnes, 1962, Westley 1957,
Westley and Tarr 1959, 1960, Collias 1970
-106-
-------
TEMPERATURE CO SALINITY (•/..)
90
SO
NOV<
HAT'
DENSITY (sigmo-t)
«tOttt4 It M 10 tt M
f
1
\ \ 1
\ \ i
N
l
* \
1
1
y \ J
t
i
i
i
t
%
\
\
\
\
»
l
i
1
1
1
l
1
1
I
1
1
l
M
ii i
i
i
\
i
N*
1
1
i
t i
i i
OXYGEN (mg-ot/1)
49 .40 JO 40
6
cs
Figure 111-12 SEASONALLY AVERAGED VERTICAL PROFILES IN
BELLINGHAM BAY
Source: compiled from Collias et al. 1966
Notation:
line Bellingham Bay
dash-dot Off Entrance Island in the Strait
of Georgia
dash New Dungeness NE in the Strait of
Juan de Fuca
-107-
-------
Notation:
line Bellingham Bay
dash-dot Off Entrance Island in the Strait of Georgia
dash New Dungeness NE in the Strait of Juan de Fuca
TOKiuruc ra shmtt nu
St.
a
IT
ft
1
I!!
so
40
90
OENSTTY (wgmo-t) OXYGEN (nq-ai/t)
CO
1
X
*
40
.MO
JM
JM
I
X
i
10'
Figure 111-13 VERTICAL WATER PROFILES DURING LOCAL
PERIODS OF HIGH (JUNEJ AND LOW (AUGUST) RIVER
INFLOW
Source: compiled from Collias & Barnes 1962,
Collias 1970
-108-
-------
The annual average discharge for the GP mill during 1966 - 1972
(before primary treatment) was approximately 49 mgd. The flow
remained nearly the same after primary treatment was installed.
This flow is equivalent to 1.75 m3s~1 or 0.055 km3 per year;
whereas the volume of the Bellingham - Samish Bay system at
MHHW is 5.3 x 109 m3 (Table III-2). Thus the annual effluent
discharge is approximately 1% of the system's volume at high
tide. The annual average discharge of the SP mill at Anacortes
after 1964 - 1978 was- approximately 6.7 mgd (Bruce Johnson,
personal communication). This flow is equivalent to approxi-
mately 0.29 m3s"1 of 0.009 km3 per year. This annual flow is
approximately i % of the volume of the Padilla - Fidalgo Bay
system at high tide. More detailed analysis of the Georgia-
Pacific effluent dilution limits are presented in Chapter VIII.
-109-
-------
REFERENCES
Baker, E.T., J.D. Cline, R.A. Freely, and J. Quan. 1978.
Seasonal Distribution, Trajectory Studies, and Sorption
cKaracteristies of Suspended Particulate Matter in the""
Northern Puget Sound Region. National Oceanic and Atmos-
pheric Administration, Pacific Marine Environmental Labora-
tory. Interagency, Energy/Environment R and D Report No.
EPA-600/7-78-126. 140 pp.
Barnes, C.A. and C.C. Ebbesmeyer. 1978. "Some Aspects of Puget
Sound's Circulation and Water Properties." IN: Estuarine
Transport Processes (B. Kjerfve, ed.), University of
South Carolina Press, Columbia, South Carolina. 331 pp.
Barnes, C.A., A.C. Duxbury, B.A. Morse. 1972. "Circulation and
Selected Properties of the Columbia River Effluent at Sea."
IN: The Columbia River Estuary and Adjacent Ocean Waters
Ta.T. Pruter and D.L. Alverson, eds.), university of Wash-
ington Press, Seattle, Washington. 868 pp.
Barnes, C.A., E.E. Collias, J.H. Lincoln, P.M. McLellan, and
M.P. Wennekens. 1956. Preliminary Oceanographic Report
of Channels through the San Juan Islands between Fidalgo
and Vancouver Islands. University of Washington Department
of Oceanography. Special Report No. 21. 163 pp.
Bartsch, A.F., R.J. Callaway, R.A. Wagner and C.E. Woelke. 1967.
"Technical Approaches Toward Evaluating Estuarine Pollution
Problems." IN: Estuaries (G.H. Lauff, ed.), American Associa-
tion for the Advancement of Science. Publication No. 83,
757 pp.
Benson, R.K., K.A. Kobe, and R.H. Scott. 1941. "Chemical Studies
of Sulfite Waste Liquor Pollution of Sea Water and Distribution
of Such Liquor Near Bellingham and Anacortes." Pacific Pulp
and Paper Industry: 15 (12).
Benson, H.K., K.A. Kobe, and R.H. Scott. 1942. "Chemical Studies
of Sulfite Waste Liquor Pollution of Sea Water and Distri-
bution of Such Liquor Near Bellingham and Anacortes." Pacific
Pulp and Paper Industry: 16(1).
Brown and Caldwell, Inc. 1976. Preliminary Design Report on
Submarine Outfall Alternatives^ Prepared for Georgia-Pacific
Corp., Bellingham Division. Confidential company document.
Callaway, R.J., J.J. Vlastelicia, and G.R. Ditsworth. 1963.
Puget Sound Oceanographic Field Studies Data Report: Everett,
Bellingham, and Port Angeles, 1962 - 1963., Unpublished
data on file at the Environmental Protection Agency, Corvallis
Environmental Research Laboratory, Corvallis, Oregon.
-110-
-------
Cannonh G.A. 1973. Observations of Currents in Puget Sound, 1970.
National Oceanic and Atmospheric Administration Technical
Report ERL 260-POL 17. 77 pp.
Cannon, G.A. (ed.). 1978. Circulation in the Strait of Juan de
Fuca; Some Recent Oceanographic Observations» National
Oceanic and Atmospheric Administration Technical Report ERL
399-PMEL 29. 49 pp.
Cardwell, R.D. and C.E. Woelke. 1979. Marine water Quality
Compendium for Washington State. Washington State Department
of Fisheries, Olympia, Washington, 2 volumes, 603 pp.
CH2M Hill. 1969. Pollution Control.for Bellingham Bay; Sewerage
Facilities Design StudyT Final Report to the City of
Bellingham, Washington and Georgia-Pacific Corporation.
CH2M Hill. 1976. Bellingham Bay Monitoring Program: A Report on
Receiving Water and Sediment Quality in the Vicinity of the
Post Point Diffuser Outfall, Bellingham Bay, Washington. Final
Report to the City of Bellingham,Washington and Georgia-
Pacific Corporation. 63 pp.
Collias, E.E. 1970. Index to Physical and Chemical Oceanographic1
Data on Puget Sound and Its Approaches, 1932 - 1966. Unlverl"
sity of Washington Department of Oceanography Special Report*
No. 43.
Collias, E.E. 1971. Currents in Bellingham Bay for the Period
17 April to 28 May 1^63. Final Report to Cornell, Howland,
Hayes and Merrifield Company, Bellevue, Washington. 10 pp.
Collias, E.E. and C.A. Barnes. 1962. An Oceanographic Survey
of the Bellingham - Samish Bay System. Volume I: P.hysical
and Chemical Data. University of Washington Department of
Oceanography Special Report No. 32. 138 pp.
Collias, E.E., C.A. Barnes, C.B. Murty, and D.V. Hansen. 1966. An
Oceanographic Survey of the Bellingham - Samish Bay System.
Volume II: Analyses of Data. University of Washington
Department of Oceanograpny Special Report No. 32. 142 pp.
Crean, P.B. and A.G. Ages. 1971. Oceanographic Records from
Twelve Cruises in the Strait of Georgia and Straxt of Juan
de Fuca, 1968. Department of Energy, Mines, and Resources,
Marine Sciences Branch, Victoria. 5 volumes.
Driggers, V.W. 1964. Tracer Dye Studies in Lake Union and Bell-
ingham Bay. M.S. Thesis. University of Washington. 73 pp.
Microfilm.
Ebbesmeyer, C.C. and C.A. Barnes. 1980 (In Press). "Control of a
fjord basin's dynamics by tidal mixing in embracing still
zones." Submitted to Estuarine and Coastal Marine Science.
-Ill-
-------
Ebbesmeyer, C.A., J.M. Cox and J.M. Helseth. 1980. "Dispersion of
Pulp Mill Effluent in Port Angeles Harbor arid Vicinity
Evans-Hamilton, Inc., Western Region (Preliminary Report).
Feely, R.A. and M.P. Lamb. 1979. A Study of the Dispersal of
Suspended Sediment from the Fraser and Skagit River Into
Northern Puget Sound Using Landsat Imagery. National Oceanic
and Atmospheric Administration, Pacific Marine Environmental
Laboratory. Interagency, Energy/Environment R and D Program
Report No. EPA-600/7-79-165. 46 pp.
Harris, R.G. and M. Rattray. 1954. The Surface Winds Over Puget
Sound and the Strait of Juan de Fuca and their Oceanographic
Effects. University of Washington Department Technical Report
No. 37.
Johnson, Bruce. 1980. Personal communication to Jeff Cox, Evans-
Hamilton,. Inc.
Johnson, G., D.R. Glick, and F.R. Foley. 1958(A). Laboratory
report - Dissolved Oxygen, SSL and Chlorinity in Inner
Bellingham Bay Over a Tide Cycle. Puget. Sound Pulp and Timber
Company. File 751.05. April 9, 1958.
Johnson, G., D.R. Glick, and F. R. Foley. 1958(B). Laboratory
Report - Dissolved Oxygen, SSL and Chlorinity in Inner
Bellingham Bay over a Tide Cycle. Puget Sound Pulp and Timb&r
Company. File No. 751.05. Report No. 1799, April 21, 1958.
6 pp. (Processed).
Knapman, Fred W. 1957. Samish Bay Survey Data^November 3, 1957
to November 24, 1957*1 Puget Sound Pulp and Timber Company
Hydrographic Survey - Samish Bay. 1 map and code page plus
17 pages of graphs. (Processed).
Knapman, Fred W. 1958(A). Samish Bay Survey Data December 9,
1957 to January 4, 19581 Puget Sound Pulp and Timber Company
Hydrographic Survey - Samish Bay. 1 map and code page plus
17 pages of graphs. (Processed).
Knapman, Fred W. 1958(B). Samish Bay Survey Data January 13, 1958
to Puget Sound Pulp and Timber Company
Hydrographic Survey- Samish Bay. 1 map and code page plus
35 pages of graphs. (Processed).
LeMier, E.H. 1962. Bellingham Bay Water Quality Studyf May -
June, 1962. Washington State Department of Fisheries Report.
Lincoln, J.H. 1977. Derivation of Freshwater Inflow into Puget
Sound. University of Washington Department of Oceanography
Special Report No. 72. 20 pp.
McKinley, W.R., D.C. Brooks, and R.E. Westley. 1959. Measurements
of Water Transport through Swinomish Slough, Washington.
Washington State Department of Fisheries Research Papers
2 (2) .
-112-
-------
Mowry, W. 1974. Water Quality Analysis - Log Pond Fill Project -
Supplemental to Project No. 145-3. Georgia-Pacific Corpora-
tion, Bellingham division intracompany memo dated 12-4-74.
National Ocean Survey (NOS). 1976. Puget Sound Approaches,
Circulatory Survey Data Report. Preliminary Phase Through
Phase III. October 1973 - April 1975. Office of Marine
Surveys and Maps, Oceanographic Division. 104 pp.
National Ocean Survey. 1980. Tide Tables 1980. U.S. Department
of Commerce National Oceanic and Atmospheric Administration.
234 pp.
Nelson, J.M. 1974. Mercury in the Benthos of Bellingham Bay,
Washington. Huxley College of Environmental Studies,
Western Washington State College. 63 pp.
Newman, R. 1973. Water Quality Analysis - Log Pond Fill Project.
Georgia-Pacific Corporation, Bellingham Division Technical
Report: Project No. 145-3.
Ochler, D.L., L. Johnson, and F.R. Foley. 1958. Laboratory
Report - Joint SSL Survey of Samish Bay on July 13, 1958.
Puget Sound Pulp and Timber Company File No. 751.05,
Report No. 1812, July 17, 1958. 3 pp. (Processed).
Overland, J.E., M.H.Hitchman, and Y.J. Han. 1978. A Regional
Surface Wind Model for Mountainous Coastal Areas. Unpublished
manuscript.
Parker, B.B. 1977. Tidal Hydrodynamics in the Strait of Juan
de Fuca - Strait of Georgia. National Oceanic and
Atmospheric Administration. Technical Report NOS 69.
Pashinski, D.J. and R.L. Charnell. 1979. Recovery Record for
Surface Drift Cards Released in the Puget Sound - Strait
of Juan de Fuca System During Calendar Years 1976 - 1977.
National Oceanic and Atmospheric Administration Technical
Memorandum ERL PMEL-14. 30 pp.
Pickard, G.L. 1975. Annual and Longer Term Variations of Deep
Water Properties in the Coastal Waters of Southern British
Columbia. Journal of Fisheries Research Board of Canada.Vol.
32: IS61-1587
Puget Sound Pacific Oyster Bulletin, 1946.
Redfield, A.C. 1950. "Note on the Circulation of a Deep
Estuary - the Juan de Fuca - Georgia Straits," IN: Proceedings
Colloquim on Flushing of Estuaries. Woods Hole Oceanographic
Institution. 175-177.
-113-
-------
Saxton, W.W. and A. Young. 1948. Investigation of Sulfite
Waste Liquor Pollution in Fidalgo and Padilla Bays. Wash-
ington State Pollution Control Commission. 25 pp.
Schumacher, J.D. and R.M. Reynolds. 1975. STD, current meter,
and drogue observations in Rosario Straxt, January - March
1974. NQAA Technical Report ERL 33.3-PMEL 24. 212 pp.
Seattle Marine Laboratories. 1974. Evaluation of the Adequacy
of the Scott Paper Company Submarine Outfall in Guemes
Channel. 63 pp.
Sternberg, R.W. 1961. "Recent Sediments in Bellingham Bay,
Washington." Northwest Science. Vol. 41(2):63-79.
Tollefson, Roger. 1962. Summary of Existing Hydrographic Data -
North Puget Sound 1953 - 19 6 IT Report to the Puget Sound
Pulp and Timber Company. 75 pp.
United States Army Corps of Engineers. 1977. Current Study of
Bellingham Harbor. Seattle District, Project Planning
Section. 28 pp.
United States Coast and Geodetic Survey. Current meter data on
file at the National Ocean Survey.
U.S. Geologic Survey. 1970-1976. Water Resources Data for
Washington. Part 1: Surface Water Records. U.S. Department
of Interior.
University of Washington Department of Oceanography. 1953.
Puget Sound and Approaches: a literature survey. Volume 1:
Climatology, p. 41-83.
Vagners, J. and P. Mar. 1972. Oil on Puget Sound: an interdis-
ciplinary study in systems engineering. Washington Sea
Grant, University of Washington Press, Seattle, Washington.
629 pp.
Wagner, R.A. and E. Ice. 1958. Guemes Channel and Padilla Bay
Float and Circulation studiei"! Washington State Pollution
Control Commission. 77 pp.
Wagner, R.A., C.D. Ziebell, and A. Livingston III. 1957. An
Investigation of Pollution in Northern Puget Sound. Wash-
ington State Pollution Control Commission Technical Bulletin
No. 22, 27 pp.
Waldichuk, M. 1957. "Physical Oceanography of the Strait of
Georgia, British Columbia." Journal of the Fisheries Research
Board of Canada. Vol 14(3).
Washington State Pollution Control Commission. 1957. Studies
of Bellingham Bay and Adjacent Waters. July 1957. 1-6
pp. plus 2 figures.
-114-
-------
Washington State Pollution Control Commission. 1967. Pollutional
Effects of Pulp and Paper Mill Wastes in Puget SouncT: a "
report on studies conducted by the Washington State enforce-
ment project.U.S. Department of the Interior, Federal
Water Pollution Control Administration. 474 pp.
Webber, H.H. 1975. The Bellingham Bay Estuary: A Natural
History Study. Huxley College of Environmental Studies.
y2 pp.
Webber, H.H. 1977. Bellingham Bay Literature Survey. Huxley
College of Environmental Studies, Western Washington State
College. 52 pp.
Webber, H.H. 1978. Studies on Intertidal and Subtidal Benthos,
Fish, and Water Quality in Bellingham Bay. Huxley College
of Environmental Studies, Western Washington University.
7 8 pp.
Westley, R.E. 1957. Washington State Department of Fisheries
Hydrographic Data Vol II, No. 6: Physical and Chemical
Data, North Puget Sound Hydrographic Trips, 1956-1957.
Washington State Department of Fisheries. 21 pp.
Westley, R.E. 1958. Observations_of Sea Water Temperature,
Density and Salinity, State of Washington 1951-1957.
Washington State Department of Fisheries Hydrographic
Data, Vol. I, No. 2. 76 pp.
Westley, R.E. 1960. "A Summary of Recent Research by the Wash-
ington State Department of Fisheries on the Distribution
and Determination of Sulfite Waste Liquor (SWL)." IN;
Reports on Sulfite Waste Liquor in a Marine Environment
and Its Effect on Oyster Larvae. Washington Department of
Fisheries Research Bulletin No. 6.
Westley, R.E. and M.A. Tarr. 1959. Physical and Chemical Data,
North Puget Sound Hydrographic Trips, 1958. Washington
State Department of Fisheries Hydrographic Data. Vol. II,
No. 1. 46 pp.
Westley, R.E. and M.A. Tarr. 1960. Physical and Chemical Data,
North Puget Sound Hydrographic Trips, 19591 Washington
State Department of Fisheries Hydrographic Data. Vol. Ill,
No. 2, 22 pp.
-115-
-------
IV. WATER QUALITY
Water quality in Bellingham Bay and surrounding marine waters is
regulated by both federal and state statutes. The Clean Water
Act of 1972 (Federal Water Pollution Control Act) arid its
amendments established national goals and objectives which include:
• eliminating pollutant discharge into navigable
waters by 1985
• protecting fish, shellfish, wildlife, and providing
for recreation through interim water quality goals
by July 1, 1983
• prohibiting the discharge of toxic pollutants in
toxic amounts
Guideline development and enforcement of these goals for indus-
trial discharges is the regulatory authority of the U.S. Environ-
mental Protection Agency (EPA).
State regulatory authority is administered by the Washington
Department of Ecology (DOE) and guidelines for water quality
standards are outlined in the Washington Administrative Code
(WAC 173-201) (DOE 1978). The parameters and standards defined
in WAC 173-201 form the basis of comparison for receiving water
quality discussed in this chapter. The main parameters discussed
will be temperature, pH, dissolved oxygen (DO), and turbidity,
in addition to spent sulfite liquor (SSL) or sulfite waste
liquor (SWL) (referred to in this chapter as SSL for uniformity)
which to some extent indicate the presence of sulfite mill
effluent constituents. State standards for the.regulated para-
meters are shown in Table IV-1. Toxic substances and complex
organic pollutants are discussed in Chapters II and V.
A. WATER QUALITY CRITERIA
The inner and outer portions of Bellingham Bay are classified by
the State of Washington as Class B and class A waters, respectively.
The inner harbor is defined as waters of Bellingham Bay:
• east of a line bearing 185° true from entrance of
boat basin (light #2)
-116-
-------
TABLE IV-1 WATER QUALITY CRITERIA FOR CLASS A AND B MARINE WATERS (Extracted from
WAC 173-201-045)
Parameter
Class A: Maximum, Minimum, Range
or Variation
Class B: Maximum, minimum, range
or Variation
Fecal Coliform Organisms
l)
Shall not exceed median of 14 organisms
per 100 milliliters (ml).
l)
Shall not exceed a median value of 100
organisms per 100 milliliters.
2)
Not more than 10 percent of samples shall
exceed 43 organisms per 100 ml.
2)
Not more than 10 percent of samples shall
exceed 300 organisms per 100 ml.
Dissolved Oxygen
Shall exceed 6.0 mg/1.
Shall exceed 5.0 mg/1 or 70% saturation
whichever is greater.
Total Dissolved Gas
Shall not exceed 110 percent of
saturation.
Shall not exceed 110 percent of satur-
ation.
Temperature
1)
Shall not exceed 16°C due to human
activity.
1)
Shall not exceed 19°C due to human
activity.
2)
No temperature increase greater than
0.3°C due to point sources.
2)
No temperature increase from human source
greater than 0.3°C when natural conditions
exceed 19°C.
pH
1)
pH shall range from 7.0 to 8.5.
1)
pH shall range from 7.0 to 8.5.
2)
Man caused variations shall be less
them 0.5 units.
2)
Man caused variations shall be less than
0.5 units.
Turbidity
l)
Not to exceed 10 percent above back-
ground (when background >50 NTU).
1)
Not to exceed 20 percent over background
(when background >50 NTU).
2)
Not to exceed 5 NTU above background
(when background <50 NTU).
2)
Not to exceed 10 NTU over background
(when background <50 NTU)•
Toxic,' Radioactive or
Deleterious material
Shall be below public health signifi-
cance or which may cause acute or
chronic toxic conditions to the
aquatic biota or adversely affect
water use.
Shall be below public health significance
or which may cause acute or chronic toxic
conditions to the aquatic biota or adver-
sely affect water use.
Aesthetic values
Shall not be impaired
Shall not be reduced or dissolved sus-
pended, floating or submerged matter
not attributed to natural causes.
-------
• east of a line bearing 142 true through fixed green
navigation light at southeast end of dock to the
east boat basin jetty
The sections designated as Class B and Class A waters are shown
on the map in Figure II-l in Chapter II.
WAC 173-201-045 (DOE 1978) defines Class B waters to have "good" water
quality. The general characteristic of Class B waters is that:
"water quality of this class shall meet or exceed the
requirements for most uses" (WAC 173-201-045)
The uses referred.to include but are not limited to:
• industrial and agricultural water supply
• fishery and wildlife habitat
• general recreation and aesthetic enjoyment (picnicking,
hiking, fishing, and boating)
• stock watering
• commerce navigation
• shellfish reproduction and rearing, and crustacean
harvesting
Class A standards require that these waters meet or exceed the
requirements for all or substantially all uses. The uses are
essentially the same for Class A waters with the addition of
domestic water supply. These uses are defined more fully for
marine waters under WAC 173-201-050 and in a report on Port
Angeles Harbor (Shea et al. 1981).
B. WATER QUALITY MONITORING
The major data base for Bellingham water quality is contained
in several 1-3 year monitoring efforts by academic institutions,
federal agencies, and staff or contractors of Georgia-Pacific
Corporation. In addition, a number of semi-permanent stations
have been run for periods of several years by EPA and oceanographic
cruises have been conducted at intervals by the University of
Washington. Various short term special studies have also been
-118-
-------
conducted; however', this data is not useful as a synoptic base,
but only for comparisons with other studies in the same area.
1. Early Studies (1950 - 1970)
Available water quality information on Bellingham Bay dates back
to studies by pulpmill personnel in the early 1950's (Tollefson
1962). The first large-scale comprehensive survey, however, was
carried out by the Washington Pollution.Control Commission CWPCC)
during the summer of 1957 (Wagner, Ziebell and Livingston 1957).
During the same period, monthly samplings were being carried out
during a 3-year period for the Washington Department of Fisheries
(WDF)(Westley 1957, Westley and Tarr 1959 and 1960, and Westley
1960) . Following cessation of the WDF program in 1959, oceano-
graphic sampling by the University of Washington was commenced
and continued for a two year period.
During the early 1960's, federal agencies, including the Federal
Water Pollution Control Commission, became involved in large
scale monitoring throughout Puget Sound and adjacent waters and
collected synoptic data on Bellingham Bay as a follow-up to the
Puget Sound Enforcement Conference (Callaway, Vlastelicia and
Ditsworth 1963, USDI 1967). These, coupled with a few short
term studies (Lemier 1962) form the pre-1970 data base for
Bellingham Bay* Little data is known to exist during the period
1965 - 1970 except that from a few STORET stations. Table IV-2
summarizes these early studies showing time periods and number of
stations. Figure IV-1 shows sampling locations for the main
long-term studies.
Tollefson (1962) reports data gathered on miscellaneous dates
by Puget Sound Pulp and Paper (now Georgia-Pacific Corporation)
over the period 1955 - 1961. In addition, he summarizes certain
studies and data gathered by WDF and the University of Washington
over the period 1953 - 1959. Much of Tollefson's reported data
is geared toward cross-checking information on Bellingham Bay
generated by WDF from split samples. Values of temperature often
-119-
-------
Table IV- 2 BELLINGHAM BAY SAMPLING STUDY SUMMARY
Study Designation and/or Author
Time Period of
Sampling
Number of
Stations
Location(s)
Tollefson 1962
Washington Pollution Control Commission
(Wagner, Ziebell and Livingston 1957)
Washington Department of Fisheries
(Westley 1960, Westley 1957,
Westley and Tarr 1959, and
Westley and Tarr I960)
University of Washington
(Collias and Barnes 1962)
Environmental Protection Agency
(Callaway, Vlastelicia and
Ditsworth 1963)
Federal Water Pollution Control Commission
(U.S. Department of Interior 1967)
CH2M Hill (1976)
1955 - 1961
1957
(summer)
September 1956
September 1959
(monthly)
November 1959
November 1961
(monthly)
1963
(summer)
October 1962 ¦
December 1964
(bi-monthly)
1972-1974
(quarterly)
July 1974-
October 1975
(monthly)
Approx. 40
50
31
27
55
17
12
Inner Harbor:and outer
bay
Inner Harbor, outer
Bellingham Bay., Samish
Bay, Padilla Bay and
Fidalgo Bay
Inner Harbor, outer
Bellingham Bay, Samish,
Padilla and Fidalgo
Bays
Inner Harbor, outer
Bellingham Bay,
Samish Bay
Inner Harbor, outer
Bellingham Bay,
Samish Bay
Inner Harbor and
Bellingham Bay north
of Post Point
Bellingham Bay
Webber (1978)
197ft
14
Bellingham Bay
-------
Anacortes
Figure IV-1 WATER SAMPLING STATIONS IN THE BELL INGHAM AREA: A. Washington
Pollution Control Commission, B. Washington Department of
Fisheries, C. University of Washington Oceanography, and
D. U.S. Environmental Protection Agency (WPCC).
Source: USDI 1967, Wagner, Ziebell & Livingston 1957
-------
vary 2-3 degrees between the two and mid-range salinities fre-
quently differ by 10 parts per thousand (ppt) as reported by WDF.
Tollefson has calculated frequencies of various SSL concentra-
tions at surface and depth stations (composite of all subsurface
samples) in three areas of the Bellingham - Samish Bay system
(Figure IV-2) as shown in Figures IV-3 and IV-4. He has also
performed a similar calculation for dissolved oxygen (DO) levels
(Figure IV-5). It can be seen from these two curves that high
SSL and low DO are closely related both qualitatively and quanti-
tatively. Values of SSL which occur roughly 10 percent of the
time in the upper bay correlate strongly with DO values less than
4.0. In the lower bay where values seldom are above 300 PBI,
DO values remain above 6.0. It should be remembered that these
trends are true only in aggregate since upwelling, winds and
other natural phenomena also affect DO values.
Studies by WPCC (Wagner, Ziebell and Livingston 1957) show similar
results to those of Tollefson in terms of salinity, temperature,
DO, and SSL. Temperature (summer) generally ranges from 12° to
15° C at bottom depths, and 17° to 20° C on the surface. Salinity
(measured as chlorinity) ranged from 8 - 16 ppt on the bottom and
3-12 ppt on the surface. DO values ranged from 0.6 to 8.5 on
the surface and 0.0 to 8.1 at depth. SSL values near the mill
were of the order of several thousand (maximum 4509 PBI) and
maximum surface values were above two hundred throughout the
sampling stations. Average surface values seldom fell below
100 ppm. All stations at which SSL exceeded 3000 ppm correlated
with average surface DO levels below 1.0 and average DO levels
at depth were uniformly 0.0.
Washington Department of Fisheries studies (Westley 1957, Westley
and Tarr 1959, 1960, Westley 1960) give data on temperature,
salinity, DO, SSL and occasionally phosphates, biochemical oxygen
demand (BOD), and wind direction and velocity. Figures IV-6
and IV-7 show annual graphs of DO and SSL for six selected stations
-122-
-------
Nooxmck: Rtvar
Strait of
Georgia
Lummi Bay (/ tomjfit
Indian
y*tion
Area A
Bettingham
m
Portage
Area B Chuckanut Bay
Pleasant Bay
tuns mi
I X M*
Eliza IsL
San Juan
Islands
Area C
vandovl
Isl
Samish Bay
Fidaigo
100 200
50 150 300
thousands of feet
Figure IV-2 THREE SAMPLING AREAS IN THE BELLINGHAM - SXMISH BAY
SYSTEM
Source: Tollefson 1962
_ 1 ^ ^ _
-------
100
90
80
T0
60
50
40
30
20
10
0
- Depth
- Surface
'I'll
350 400 450 500
Spent Sulfite |ppm|
1 n
50
re IV-3
100
150
I
200
250
I
300
T
CUMULATIVE PERCENTAGE FREQUENCIES OF SPENT SULFITE
LIQUOR (SSL) IN BELLINGHAM BAY NORTH OF POST POINT
AND POINT FRANCES (Area A on Figure IV-2)
Source: Tollefson 1962
-124-
-------
E 100
&
a ¦
Depth
Surface
90-
70
40
20
0
100
50
500
150
200
350
450
250
300
400
Spent Sulfite |ppm|
Figure IV-4 CUMULATIVE PERCENTAGE FREQUENCIES OF SPENT SULFITE
LIQUOR (SSL) IN BELLINGHAM BAY BETWEEN POST POINT AN
GOVERNORS POINT TO ELIZA ISLAND (Area B on Figure
IV-2) Source: Tollefson 1962
-125-
-------
100
90
80
70
60
50
40
30 •
20
10 «
0 1
Area B//Area C
re IV-5
T | I I 1
9 10 11 12 13
Dissolved Oxygen {ppm|
CUMULATIVE PERCENTAGE FREQUENCY OF DISSOLVED OXYGEN
(composite) for: A. Area north of Post and Francis
Points, B. Area between Post and Governors Points
and Eliza Island, C. Area south of Governors Point
including Samish Bay. See Figure IV-2.
Source: Toliefson 1962
-126-
-------
12.Q.
11.Q.
iaa
9LQ
8£
7.g
-«.a
g
a
a
o
d s-qj
~•ft
xa
2.1
key:
—— - Station 1
—— — Station 5
f\
1939
1957
1988
1090
Figure IV-6a. 00 LEVELS RECORDED AT STATIONS 1 AND 5, 1956-1959
Source: Westley 1957, Westley and Tarr 1959, 1960
-127-
-------
KEY
Station 3
Station 3A
1.4
1956
1987
IMS
1980
Figure IV-6b. DO LEVELS RECORDED AT STATIONS 3 AND 3A, 1956-1959
Source: Westley 1957, Westleyand Tarr 1959, 1960
-128-
-------
12.Q,
11.^
io.a
8£
7.1
• key:
— - Station 15
— - Station 17
—®-(l
E
a
a
SM!
*0.
3-a
a Ji
I.Q.
J M M J S N
1988
J M M J S N
1987
J M M J S M
1958
J M M J S N
1989
Figure IV-6c. DO LEVELS RECORDED AT STATIONS 15 AND 17f 1956-1959
Source: Westley 1957, Westley and Tarr 1959, 1960
-129-
-------
- Stmiwi 5
- SMtlOfl s
- Vrti* common la
both station*
WT
1>M
Figure IV-7a TIME HISTORY OF SSL LEVELS AT SELECTED STATIONS.
Source*. Westley 1957, Westley and Tarr 1959, 1960
-130-
-------
1Q00Q
IjOOQ
10Qj
1
a
a
KEY:
— Station 3
- SUtlon M
J P II AM J j ABOWpj > MA MJ j A S ON p J M>MJ J A 8 0 h"
FIGURE IV-7b TIME HISTORY SSL LEVELS AT SELECTED STATIONS
Source: Westley 1957, Westley and Tarr 1959, 1960
-131-
-------
KEY:
- Station IS
Station 17
1Qfi
Figure IV-7C TIME HISTORY OF SSL LEVELS AT SELECTED STATIONS
Source: Westley 1957, Westley and Tarr 1959, I960
132-
-------
in Bellingham and Samish Bays. Figure VIII-18 locates the six
stations. Although variations in winds are not factored out in
these figures, wind direction is an important factor in the Bell-
ingham system (Westley 1960) in terms of both surface distributions
and vertical mixing.
SSL values tend to be highest at Stations 2, 3, 5 and 6. These
stations had SSL values in excess of 200 ppm (sometimes to 6000 ppm),
at relatively frequent intervals, and DO levels which drop below 5
ppm (occasionally to zero). These four stations (with the excep-
tion, of Station #1, which is in the Nooksack freshwater plume)
are the northern bay stations closest to the City of Bellingham
and the mill. During 1956 - 1958, SSL values tended to be highest
in the period June - December. Occasionally there would be periods
during this time when values at all stations were close to zero..
This probably indicates effects of winds dissipating the effluerst
to the southwest and out of the Bellingham system. In 1959,
however, SSL values were also high during the spring months.;
These occurred during a period when the winds were calm or weak
out of the south or southeast, a pattern which was not normal
compared to spring winds of 1957 - 1958 (which were generally 5-25
knots from the north).
University of Washington (UW) studies (Collias and Barnes 1962)
began 2 months after the cessation of the WDF effort. Unfortunately,
there were some changes in station locations and several changes
in methodology, so that the data cannot be interpreted as a 4 - 5
year data set. Some station locations do overlap with the pre-
vious WDF studies. Techniques for measuring SSL, however, were
altered based on a modified procedure for PBI developed in 1959.
The result of changing stations and PBI methods seems to be that
the data values for SSL were considerably lower in the University
of Washington data, seldom exceeding 100 ppm with highest values
only in the range of 200 - 400 ppm. This is roughly an order of
magnitude difference from WDF maximum values.
-------
Since none of the UW studies are in close proximity to the mill,
the DO values less than 4 mg/1 found in WDF studies are not found
here, except in bottom waters. In general, surface water DO
exceeded 5.0 mg/1 most of the time at the stations sampled.
Occasionally, a PBI reading of 200 or more is correlated with a
DO reading below 4.0 mg/1 (i.e. 7/19/60 when surface SSL = 313 and
DO = 2.67 at station BLL005). Bottom waters below 20 meters
frequently have DO values near or below 4.0 mg/1 according to
the UW data. Comparisons between surface DO patterns found during
WDF and UW sampling are shown in Chapter VIII.
Phosphates in the bay generally ranged from 0-3.5 mg/1 at the
stations measured. This range is fairly normal for areas of Puget
Sound near a major estuary.
in another study (Collias 1971), University of Washington personpe^L
measured current patterns at 10 locations in the bay during April *
and May 1963. This is discussed above in Chapter III.
During the period 1962 -1964, the Puget Sound Enforcement Confer-
ence conducted extensive water sampling by the Federal Water
Pollution Control Commission (WPCC), forerunner to the U.S.
Environmental Protection Agency (Callaway, Vlastelicia and Dits-
worth 1963, USDI 1967). Sixteen cruises were made from October
1962 to December 1964 with sampling at 17 stations for temperature,
pH, salinity, DO, SSL and water clarity. Miscellaneous tests
were also run for chlorophyll, total volatile solids and other
parameters.
These federal studies found conditions similar to those reported
by WDF with inner harbor SSL values ranging up to 6000 ppm and
surface DO values sometimes depressed below 4.0 mg/1. Surface
pH was typically between 7.8 and 8.3 in the northern portion of
Bellingham Bay, decreasing toward the north and east (mill lo-
cation) with surface pH as low as 6.0 next to the Georgia-Pacific
mill (see Figure IV-8). Data was also taken on juvenile salmon,
-134-
-------
A. Surface pH
B. Surface pH
Figure IV-8. SURFACE pH DISTRIBUTIONS IN A. NORThEwT BELLINGHAM BAY, AND
B. VICINITY OF GEORIGA-PACIFIC PULPMILL ON MAY 26, 1964
Source: USDI 1967
-------
Oysters and bottom dwelling organisms in these studies. Results
are reported in Chapters V and VI.
Lemier (1962) conducted a short term water quality study during
May and June 1962,concentrated in Northern Bellingham Bay. Lemier
sampled 5 stations for SSL, chlorinity, temperature, and DO. He
found ranges of 1992 -5802 ppm SSL correlated with 00 values of
0.0 mg/1 near the mill. Other station SSL values ranged from
6 - 504 ppm with corresponding DO values between 4.7 and 10.5.
Lemier took only 4 samples at each station in an attempt to
correlate mill effluent with effects on chinook salmon (live box
studies described in Chapter V).
After the completion of the federal (USDI 1967) and state (Lemier
1962) studies in the early 1960's, no major programs for water
quality sampling were carried out on the Bellingham area until
the implementation of primary treatment requirements in 1970 - 1917$.
Thus the only monitoring during the period 1964 -1970 is from
miscellaneous samplings and cruises reported on the STORET system
(see section on STORET monitoring below).
2. Recent Studies (1971 - present)
Most of the post-1970 data on Bellingham Bay has been gathered by
CH2M Hill Corporation under contract with Georgia-Pacific and
the City of Bellingham. These studies included biweekly (March -
November) and monthly (December - February) sampling in Bellingham Bay
(1972-1975)(CH2M Hill 1976) supplemented by occasional studies
related to dredging impacts (Newman 1973). In addition, two
environmental impact statements (U.S. Army Corps of Engineers
1975, City of Bellingham 1978), and another study conducted for
the Corps by Western Washington university (Webber 1978) summarize
most of the relevant post-primary treatment data. No appreciable
studies of the post-secondary treatment period (1979 - present)
are currently available.
-136-
-------
The CH2M Hill monitoring study (July 1972 -October 1975) was con-
ducted in the vicinity of the Post Point Sewage Treatment Plant
(STP) diffuser outfall. Data was collected both previous and
subsequent to the installation of primary facilities at the Post
Point STP (September 1974). Initially seven fixed stations were
monitored with a floating location designated as Station 8
(Figure IV-9). Stations 4 and 4a were used as water quality
and benthic control locations, respectively. Beginning in July 1975
through October 1975 stations 3, 5, 6, and 8 were discontinued and
replaced with stations 9, 10, 11, 12, B1 and B2 (Figure IV-10).
Available information indicates that only bacteriological data was
collected at beach stations (Bl, B2); therefore data from these
locations are not discussed in this report.
Each water quality station was monitored for oceanographic para-
meters, chlorophyll, nutrients, coliform bacteria, benthic inverte-
brates, SSL, and various metals, usually including copper, lead, i *
zinc and mercury. The data show significant time variations for
pH, SSL and DO, most significant in surface and near surface
waters. Table IV-3 summarizes 40 months of surface data for
selected stations during the period July 1972 October 1975.
CH2M Hill also sampled six stations near the Georgia-Pacific
log storage pond at the outlet of Whatcom Creek. This
sampling was related to a proposed dredge and dredge disposal
project on the log pond (Newman 1973). The sampling concluded
that the dredging affected DO in the waterway significantly,
but other parameters were unaffected. Sulfide levels also dropped
radically part-way through the sampling but this was thought to
be unrelated to dredging operations.
Environmental Impact Statements on the expansion of Squalicum
Boat Harbor (U.S. Army Corps of Engineers 1975) and the Georgia-
Pacific secondary treatment lagoon (City of Bellingham 1978)
contain only data from a few samples each, concentrating on
constituents of dredged material rather than general water quality.
-137-
-------
Strait q1
Georgia
Lummi Bay
Cam6
-------
Strait of
Georgia
aMMM
X Outfall 91
Eliza
Cartar
Pt.
Sinclair
wmssM
San Juan
islands
Clark
FMalgo
Bay
Padilla Bay
100 200
50 150 300
thousands of feet
Figure IV-10 STATIONS MONITORED BY CH2M HILL, July 1975
October 1975
Source: CH2M Hill 1975
-139-
-------
TABLE IV-3 SUMMARY OF SURFACE WATER QUALITY PARAMETERS FOR CH2M HILL DATA AT
SELECTED SITES (July 1972 - October 1975)
1972
1973
PH
D.0. ppm
SSL ppm
PH
D.O. ppm
SSL ppm
Station
R M
R
M
R M
R M
R M
R M
1
N/D
7.6-10.4
8.8
2-280 85.4
N/D
7.8-11.0 9.7
4.5-320 63.8
2
N/D
6.6-12.5
9.3
0-245 37.8
N/D
5.5-120 9.9
4.0-359 51.5
3*
N/D
7.0-12.0
9.5
2.18 10.5
N/D
8.4-13.2 10.9
<1-48 12.3
4
N/D
7.0-11.3
8.9
1-11 6.8
N/D
7.6-13.8 10.2
<1-39 14.4
4A
N/D
8.2
2-15 8.5
N/D
N/D
N/D
5*
N/D
7.0-12.0
9.3
0-214 58.0
N/D
8.4-14.6 10.3
3-187 52.5
6*
N/D
6.0-10.4
8.7
1-450 99.8
N/D
6.2-13.0 9.8
<1-240 68.5
7
N/D
6.5-13.6
8.3
19-200 103.8
N/D
2.6-11.5 9.5
15-333 75.0
8*
N/D
4.8-11.4
7.9
11-512 95.4
N/D
5.8-13.9 7.5
44-456 113.6
g**
N/A
N/A
N/A
N/A
N/A
N/A
10**
N/A
N/A
N/A
N/A
N/A
N/A
11**
N/A
N/A
N/A
N/A
N/A
N/A
12**
N/A
N/A
N/A
N/A
N/A
N/A
continued
R = Range ^Discontinued monitoring in July 1975,
M - Mean Began monitoring in July 1975.
ppm = parts per
million
N/A = Not applicable
N/D = No data
-------
Table IV-3 Continued
1974 1975
Station
PH
D.O. ppm
SSL
ppm
PH
D.O.
ppm
SSL ppm
R M
R M
R
M
R
M
R
M
R M
1
7.5-8.0 7.7
5.2-11.8 9.7
3-211
69.8
6.6-8.3
7.5
7.3-12.2
9.7
19-330 96
2
7.6-8.1 7.8
7.6-12.8 10.1
<1-209
28.9
7.0-8.6
7.9
6.5-16.4
10.5
1-430 46.9
3*
7.5-8.0 7.8
8.4-13.6 10.4
<1-79
14.9
7.1-8.5
7.5
9.2-14.0
11.3
<1-37 11.1
4
7.5-7.9 7.7
8.1-12.4 9.7
<1-28
8.5
7.2-8.2
7.8
7.2-73.6
10.1
6-38 12.6
4A
N/D
N/D
N/D
N/D
N/D
N/D
5*
6.4-8.0 7.6
6.4-12.0 9.9
4-142
41.7
7.1-8.2
7.6
9.0-12.8
10.3
5-109 67.0
6*
7.5-8.0 7.7
7.0-12.0 10.0
7-132
38.8
7.5-8.4
7.8
8.9-12.4
10.5
14-163 118.9
7
7.4-7.9 7.7
7.0-11.8 9.7
10-140
45.2
7.2-8.3
7.8
7.8-13.2
10.2
8-280 128.4
t
8*
7.6-7.7 7.7
7.7-11.8 9.9
13-251 112.7
6.6-8.2
7.2
7.7-12.0
10.0
2-646 140.5
9**
N/A
N/A
N/A
7.9-8.3
8.0
7.0-12.1
9.2
N/A
H
1
10**
N/A
N/A
N/A
7.7-8.3
8.0
6.7-12.2
10.0
N/A
11**
N/A
N/A
N/A
7.8-8.3
8.0
7.4-16.8
10.3
N/A
12**
N/A
N/A
N/A
7.6-8.4
7.9
6.2-12.9
10.0
N/A
R = Range *Discontinued monitoring July 1975 N/A = Not applicable
M = Mean **Began monitoring July 1975 N/D =» No data
ppm - parts per million
-------
Webber (1978) has reported the moat recent survey of Bellinghaxn
Bay water quality. The study involved 14 sampling sites in inner
Bellingham Harbor for water quality, fish and benthic data.
Webber found salinity to vary greatly among his sampling sites
due to riverine stream and industrial water inflow; however, bot-
tom salinities were moderately stable. 00 values ranged from
0.0 -9.0 mg/1 with all stations recording values below saturation
during some of the readings. Lowest DO readings occurred in
Whatcom Waterway with low values occurring in both surface and
bottom waters at various times. Stations near Squalicum Creek
also report DO values significantly below 4.0 mg/1 during several
samplings.
Total suspended solids generally ranged from 0.002 to 0.015 mg/1
solids with no distinct seasonal patterns. Turbidity ranged from
0.5 NTU in the Bay to 22 NTU in Whatcom Waterway. pH values
were similar to those documented by EPA studies in the 1960's in
most of the upper bay ranging from 7.0 to 8.1. However, samples
taken in the Whatcom, and I and J Waterways were consistently
below 7.0 with a value of 2.5 in Whatcom Waterway at one sampling
time. Such strong acidity is extremely rare in seawater which is
normally buffered effectively by the high content of ionizing
salts. Sulfur was measured as sulfide rather than SSL, and all
values were reported to be less than 1 ppm.
3. STORET Monitoring
The EPA data acquisition, storage and retrieval system (STORET)
contains long-term water quality data both from large scale
studies and miscellaneous monitoring. In addition to data from
studies discussed above, the bulk of time-sequence information
is available for only a small number of stations in Bellingham
Bay. The bulk of this recent data is from 7 stations maintained
by DOE between 1968 and the present. Of these stations, three
apparently were discontinued during 1975 and 1977, and only four
(BLL006, BLL008, BLL009, and BLL010) continue to the present.
Stations BLL008, BLL009, and BLL010 monitor in the northern and
-142-
-------
central portions of Bellingham Bay and only station BLL006 is
located nea.r Bellingham (Figures IV-11 , IV-12 , IV-13 ) . These
long term stations have the best time sequence data base avail-
able on the Bay; however, several of the stations have data
gaps of several years during the period 1970 - 1975v
At this writing, data from four of the stations are available
through October 1979; however, only 3-4 readings have been taken
since the installation of secondary treatment. Insufficient
data is available as yet to make pre- and post-secondary treatment
comparisons. This is further complicated by the fact that
effluent spills have occurred subsequent to secondary treatment
installation. Time sequence data of SSL from selected STORET
stations is shown in Figures IV-14 and IV-15 . Table IV-4 sum-
marizes yearly ranges and means of the five stations for SSL and
DO.
-143-
-------
BLL004 •
*
Bellingham
Bay
*?
/y
/
/
BLL006'
Bellingham
4?
4/\
$.// WBLL001;
jfr/' 011115^
& BLL002
48° 45'
/
/
rf
&
/
/
48°44'
0 200 400 750 yawto
100 300 500 1000
122*30'
122*29'
Figure IV-11 MAJOR STORET STATIONS: INNER BELLINGHAM HARBOR
Source: EPA STORET System, unpublished data
-144-
-------
0 1000 2000
500 1900 3000 yards
1221315
Bellingham
012307
48 45
BLL780
011331 •
Bellingham
Bay
see fig
IV-11
BLL783* L—
BLL007^
013916 ^
BLL755#
BLL008P
South
Bellingham
Pt. Frances
BLL009#
012217
Chuckanut
Bay
012524#
012417 •
48°40
122 30
Figure IV-12 MAJOR STORET STATIONS: NORTHERN BELLINGHAM BAY
Source: EPA STORET System, unpublished data
-145-
-------
Strait of
Georgia
BelUngham
011644
012731
•BU.01O
013236
Balllngham Bay
012134*
San Juan
Islands
013505#
• 013926
014035
° "SAM002
• 014115
• PAD721
•014629
•011620
0
Anacortes
122 50'
122°30'
122 40
100 200
SO 150 300
thousands of fs«t
c
Figure IV-13 MAJOR STORET STATIONS: ROSARIO APPENDAGE
Source: EPA STORET System, unpublished data
)
-146-
-------
- BL1008
to both itallom
\f'\
\to itmt fntwal
Ms
TTTTTiTTTTTTT
JUL
JISl
i»«o
JUL
JUL
JUL
J1IL
JUL
Figure IV-14a TIME HISTORY OF SPENT SULFITE LIQUOR LEVELS AT SELECTED STORET STATIONS
Source: Unpublished STORET data
-------
¦t*
CO
1
KEY:
i ¦ ¦ J I ili
r« ¦ j iiitt] ; a
Figure IV-14b TIME HISTORY OF SPENT SULFITE LIQUOR LEVELS AT SELECTED STORET STATIONS
Source: Unpublished STORET data
-------
Table IV-4 SUMMARY OF SURFACE WATER QUALITY PARAMETERS FOR STORET. DATA AT SELECTED STATIONS (196E - 1973)
Station
Parameter
Range
or Mean
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
1979
BLL006
PH
R
iJ
-
-
-
-
-
-
-
-
-
-
-
D.O.(ppo)
n
R
7.6-10.6
3.6-8.5
4.3-10.4
-
_
_
-
-
6.7-9.9
6.5-10.5
3.4-13.1
7.9-11.5
N
8.64
7.1
7.56
-
-
-
" -
3.6
7.9
8.9
9
9.5
SSL (ppm)
R
10-185
1-1820
7-400
-
-
-
-
19.7-28
8.2-29.9
27.3-11.7
7.6-25.6
N
102
263.6
136.6
-
-
-
-
28.5
23.2
19.2
22
18.5
BLL008
R
ii
-
-
-
-
-
-
-
-
-
-
-
-
D.O. (ppm)
n
R
8.4-10.4
6.3-9.5
7-10.3
_
_
9.2-11.8
8.5-10.7
7.1-10.4
7.1-10.3
8-12.3
8-12.7
8.6-11.4
H
9.4
8
8.3
-
-
10.6
9.7
8.8
8.5
9.5
10.6
10
SSL (ppn)
R
3-63
8-120
2-170
-
-
18-23
0-23
8-86
122-14
0-77
0-23
5-27
N
28.3
32.2
64
-
-
21.3
12
42
65.2
33.8
10.6
11.5
BLL009
pH
R
ftfl
-
-
-
-
-
-
-
-
-
-
-.
D.O.(ppm)
n
R
9.2-10.8
7.7-10.5
6.3-10.6
_
_
_
.
-
_
-
8.4-12.8
6.9-12.6
N
10.3
8.8
8.9
-
-
-
-
-
-
12.3
10.9
9.6
SSL (ppm)
R
1-62
1-106
0-39
-
-
-
-
-
-
-
23.2-29.7
6.7-11.1
H
24
37
18
-
-
-
-
-
-
27.3
26.9
9.6
BLL010
PH
R
hi
-
-
-
-
-
-
-
-
-
-
-
-
D.O. (ppm)
n
R
8.8-10.4
6.8-10.2
6.6-9.6
_
-
_
_
-
8.5-10.8
7.8-10.5
8.6-12.8
6.9-11.9
M
9.4
8.4
8.5
-
-
-
-
9.6
9.5
10.5
9.1
SSL
R
4-19
2-128
0-12
-
-
-
-
-
-
0-18
5-14
0-14
N
12.6
15.8
5.5
—
-
—
—
—
9
8.6
8.2
- « no data
Source: EPA STORET System
-------
references
Callaway, R.J., J.J. Vlastelicia, G.R. Ditsworth. 1963. Puget
Sound Oceanographic Field Studies Data Report. Bellinqham
and Port Angeles. 1962 - 1963. EPA-660l3-73-(!)l4.
CH2M Hill. April 1976. Bellingham Bay Monitoring Program. A
Report on Receiving Water and Sediment Quality in the
Vicinity of the Post Point Diffuser Outfall, Bellingham Bay,
Washington.
City of Bellingham, Washington. March 1978. Final Environmental
Impact Statement; Georgia-Pacific Corporation Bellingham
Division"! Gregory Waddell Planning Director. 205 pp.
Collias, E.E. 1971. Current Measurements in Puget Sound and
Adjacent Waters, July 1948 - November 1955. University of
Washington, Department of Oceanography. Technical Report No.
271.
Collias, E.E. and C.A. Barnes. August 1962. An Oceanographic
Survey of the Bellingham - Samish Bay System. Volume 1s
Physical and Chemical Data. University of Washington,
Department of Oceanography. Special report No. 32. 138 pp
LeMier, E.H. July 1962. Bellingham Bay Water Quality Study,
May - June 1962. Washington State Department of Fisheries.
9 PP.
Newman, R. 1973. Water Quality Analysis - Log Pond Fill Project,
Georgia-Pacific Corporation, Bellingham Division. Technical
Report Project No. 145-3.
Shea, B.G., C.C. Ebbesmeyer, Q.J. Stober, K.L. Pazera, J.M. Cox,
J.M. Helseth and S, Hemingway. 1981. History, Dispersion
and Effects on Receiving Waters of Pulpmill Effluents: Port
Angeles, Washington (Final Report). Northwest Environmental
Consultants, Inc. 507 pp. + Appendices.
Tollefson, Roger. 1962. Basic Biological Productivity -
Bellingham Bay. March 1959 - July 1961. A Report to
Puget Sound Pulp and Timer Company. 128 pp.
Tollefson, Roger. 1963. "Basic Biological Productivity In
A Marine Industrial Area." J. Water Poll. Control Fed.
Vol. 35:989-1005.
U.S. Army Corps of Engineers. 1975. Draft Environmental State-
ment, Squalicum Small Boat Harbor"Expansion, Bellingham^
Washington. 56 pp. ~
U.S. Congress (95th), First Session. December 1977. The Clean
Water Act Showing Changes Made by the 1977 Amendments.
Serial No. 95-12. U.S. Government Printing Office, Wash-
ington D.C. 125 pp.
-150-
-------
U.S. Department of Interior. March 1967. Pollution Effects of
Pulp and Paper Mill Wastes in Puget Soundl Washington State
Enforcement Project. 474 pp. !
U.S. Environmental Protection Agency. STORET System unpublished
data.
Wagner, R.A., C.P. ziebell, and A. Livingston III. 1957. An
Investigation of Pollution in Northern Puget Sound. Washing
ton Pollution Control Committee Technical Bulletin No. 22:
1-27.
Washington State Department of Ecology. January 1978. Chapter
173-201 WAC Water Quality Standards for Waters of the State
of Washington.
Webber, H.H. June 1978. Studies on Intertidal and Subtidal Benthos,
Fish and Water Quality in Bellingham. Huxley College,
Western Washington University. Bellingham, Washington. 78 pp.
Westley, R.E. December 1957. Physical and Chemical Data North
Puget Sound Hydrograyhic Trips 1956 and 1957. Washington
Department of Fisheries Hydrographic Data Vol II. No. 6.
Westley, R.E. 1960. Observations on Physical and Chemical Waters
Characteristics of Bellingham and siunish Bays. IN: Research
Bulletin No. 6. Washington State Department of Fisheries.
pp. 65-70.
Westley, R.E. and M.A. Tarr. March 31, 1959. Physical and
Chemical Data North Puget Sound Hydrographic Trips 1958.
Washington Department of Fisheries Hydrographic Data
Vol. III. No. 1.
Westley, R.E. and M.A. Tarr. December 1960. Physical and Chemical
Data North Puget Sound Hydrographic Trips 1959. Washington
Department of Fisheries Hydrographic Data. Vol. Ill, No. 2.
-151-
-------
V. TOXICITY
Chapter II discussed the biologically toxic compounds of bleached
sulfite mill effluent (BSME). A list of the BSME constituents
discharged by Georgia-Pacific in Bellingham have been shown in
Table II-8v Those which are known or suspected of being toxic
are listed in Table ir-7. The purpose of this chapter is to
discuss the impact of these toxic components on aquatic life.
The gross toxicity of BSME can be measured on whole effluent as
it is discharged from the mill or specific toxicity of the
individual components may be determined, provided that chemical
separation is possible. The gross toxicity of BSME discharged
from the Bellingham mill has received only limited testing. Bio-
monitoring of the receiving waters has received considerable
attention in the last 2 decades by state agencies. This section
of the report will present a brief review of the recent liter-
ature on sulfite effluent toxicity, gross toxicity bioassays
of Georgia-Pacific effluent, receiving water bioassays and the
major known or suspected biologically toxic effects of effluent
components applicable to the Georgia-Pacific mill in Bellingham.
A. LITERATURE REVIEW OF SULFITE MILL EFFLUENT TOXICITY
The conventional calcium-base sulfite pulping process is used
by Georgia-Pacific in which the digestion chemicals are not
generally recovered, but are dumped as spent sulfite liquor (SSL).
This waste has a typically high biochemical oxygen demand (BOD)
which must be considered in order to distinguish the difference
between death by asphyxiation and toxicity. Walden et al. (1975)
compared the bioassay procedures for testing pulp mill effluents.
The high oxygen demand of these test solutions necessitate
oxygenation to maintain adequate oxygen levels for fish respira-
tion during testing. Aeration may result in depletion of the
unstable toxic constituents. Walden and McLeay(1974) determined
that this volatile loss could be minimized by introducing air
in fine bubbles which could be assimilated in the test solution.
-152-
-------
Assessment of the toxicity of pulp mill wastes is complicated
by the large variability of mill effluents. Variability between
pulpmill effluents from different mills is significant even
when both use the same basic process (see Figure V-l). Within
auiy given plant, there are typically variations of effluent
constituents on a daily or hourly basis related to mill operation
changes. Therefore, a large number of bioassay tests must be
performed before reliable results can be achieved.
When only a few samples are available the operational condition
(spills, process, etc.) of the mill should be known. The addi-
tion of specific pulping chemicals such as anti-foam agents,
anti-pitch agents, sizings, biostatic agentsT etc., should
be known. The change in quantity and quality of the effluent in
a relatively short time period cam alter the validity of toxicity
values. Chemical assays are not yet feasible as a technique
for assessing toxicity of pulpmill effluents because some toxi-
cants have not been identified. In addition, the special problems
posed in the conduct of routine bioassays are discussed in
Appendix E.
Recent 96-hour LC50 toxicity data review by Hutchins (1979) on
whole suifite-mill effluents (SME) and SSL are included in
Table V-l. Data on both types of effluent are included because
SSL contains most of the toxic constituents present in whole
effluent. The SSL stream is many times more toxic them the
whole sulfite mill effluent (SME) with the exception of bleaching
effluents, inclusion of other process streams usually lowers
the toxicity of SSL (Wilson and Chappel 1973).
The 96-hour LC50 concentrations are expressed as percent by
volume because the concentration of toxic materials is usually
not known. Water use in relation to the volume of wood pulped
will determine the concentration of toxic components. In some
cases the concentration of sulfite mill effluent has been
expressed in mg/1 based on the Pearl Benson Index (PBI) which
-153-
-------
1 I ¦ I I I I I I
"IVWU0N8V lN30d3d
Figure V-l PERCENT LARVAL ABNORMALITY VS. SWL FOR THE BELLINGHAM -
ANACORTES AND PORT ANGELES AREAS.
Source: USDI 1967
-154-
-------
Table V-l ACUTE EFFECTS OF SME AND SSL ON AOUATIC LIFE
Source: Hutchins 1979
Effluent
Type
Species
96-hr LC50
(% by volume)
Comments
Reference
SME Pacific salmon
Pacific salmon
Atlantic salmon
Atlantic salmon
Atlantic salmon
SSL Pacific salmon
Pacific salmon
Rainbow trout
Rainbow trout
Rainbow trout
Rainbow trout
Atlantic salmon
2
3-45
25 - 60
11 - 24
15
0.7 - 1.45
2,340 mg/1 (PBI)
3,000 mg/1 (PBI)
0.18 - 0.29
1.1 - 3.5
8-12
2,500 mg/1 (PBI)
Untreated, Na and Ca base mills
Untreated Mg base
Untreated, Na base, high yield
Untreated, Na base, low yield
NH4 base including bleachery wastes
Neutral sulfite semi-chemical process
Aged 5 days
Samples limited to red liquors, NH4 base
Samples limited to red liquors, Mg base
Main sewer
Rosehart et_ al^. 1974
Rosehart et al. 1974
Wilson & Chappel 1973
Wilson & Chappel 1973
Wilson & Chappel 1973
Rosehart et al^ 1974
Kondo et al. 1973
Wilson 1972
Grande 1964
Wilson & Chappel 1973
Wilson & Chappel 1973
Wilson 1972
-------
is an indication of the amount of lignin present. The PBI is
limited in that it measures only a group of compounds which in
itself contribute little to the toxicity (Walden and McLeay
1974). Data for BSME is very limited; however, it is known that
the bleaching process results in increased toxicity (Hutchins
1979) .
Acute toxicity of whole sulfite effluent to juvenile Pacific
salmon (Oncorhynchus spp.) and Atlantic salmon (Salmo salar) has
been reported at concentrations as low as 2-3 percent v/v;
however, many 96-hour LC50 values have been reported between 20
and 60 percent (Table V-l). Effluents from NH4~base mills are
usually not appreciably more toxic than those from Na-f Ca- or
Mg-base mills (Rosehart ejt al. 1974) . However, effluent from
an NH^-base mill utilizing a bleach process was five times as
toxic as unbleached NH4-base sulfite effluent (Wilson and Chapp^l,
1973). Lagoon treatment lowered the toxicity of whole effluent
(including bleaching effluent) to near that of unbleached raw
effluent.
The investigation of sublethal effects is an effort to determine
a threshold level of exposure to a toxicant below which no
effect can be observed. Sprague (1971) reviewed general pro-
cedures for sublethal effects measurements and discussed the
problem of ascertaining "safe" levels for pollutants.
Known sublethal effects of pulp and paper effluents are attributed
to conifer fibers, volatile reduced-sulfur compounds and non-
volatile soluble toxic components. Recent data reviewed by
Hutchins (1979) relating to sulfite wastes are compiled in
Table V-2. The table is arranged by physiological effects.
Because of the large variation in toxicity of pulp mill effluents,
sublethal effects are expressed as a fraction of the LC50 value
for that organism. Sublethal effects of sulfite wastes have
received liiuited attention compared to kraft wastes. The sub-
lethal concentrations of SME and SSL reported in the literature
-156-
-------
Table V-2 SUBLETHAL EFFECTS OF SULFITE MILL EFFLUENTS ON AQUATIC LIFE
Source: Hutchins 1979
Threshold Concentration
Effects
Species
Eff.
Type
Fraction
of 96-hr
LC50
Volume
Comments
Reference
Respiratory
Oxygen uptake
increased
Pontogamnarus
SME
12 LC50 independent of life stage
Gazd. 1971 a,b
Salmonids
SSL
>1.0
100
Williams gtal.1953
Circulatory
Blood values
Rainbow trout
SME
Abstracted article
Seppovaara 1973
reduced
Carp
SME
Abstracted article
Seppovaara 1973
Pontogammarus
SME
12 - 25
Increased respiratory quotient
Gazd. 1971 b
Metabolism
Swimming ability
reduced
Pontagammarus
SME
12 - 25
Abstracted article
Gazd. 1971 a,b
Behavior
Avoidance
Salmonids
SSL
Avoid low but not high concen-
tration
Gazd. 1971 a,b
Feeding reduced
Pontagammarus
SME
12 - 25
LC50 independent of life stage
Gazd. 1971 a,b
Morphology, Histology
Abnormalities
increased
Oyster larvae
SSL
6-12 mg/1
(PBI)
20% increase in abnormalities
WoeIke 1960
ii
Clam larvae
SSL
—-
1-3 mg/1
(PBI)
20% increase in abnormalities
Woelke et al. 1970
M
Oyster larvae
SSL
0.15-0.5
Mg base most toxic (untreated
effluent)
Woelke et al. 1970,
1972
Growth
Growth rate reduced
Green algae
SME
15
Abstracted article
Seppovaara &
Hynninen 1970
Eff. = Effluent
Gazd. = Gazdziauskaite
-------
usually have not been related to lethal concentration as has
been the case with kraft wastes. Therefore, sublethal concentra-
tion of SME and.SSL in Table V—2 are expressed as either percent
by volume or by the Pearl Benson Index (PBI).
Williams et al. (1953) described the sequence of effects of
acutely toxic concentrations of SSL on fish prior to death. Many
of these syndromes have been observed by others during sublethal
tests. An abstracted article by Seppovaara (1973) reported that
"blood values" of rainbow and carp were reduced by sublethal
levels of SME; however, the concentrations were not given. In
another paper he reported the production of green algae was re-
duced by concentrations greater than 15 percent of SME (Seppo-
vaara and Hynninen 1970).
Gazdziauskaite (1971 a, b) studied the effects of SME on fresh- '
water shrimp (Pontogammarus). He observed reduced growth at 1.3
percent, reduced reproduction at 3-12 percent and at 12-25 per-?
cent: increased respiration rate, reduced feeding behavior,
reduced "blood values" and in some cases immobilization. Growth
was the most sensitive index. Although production-abundance data
are available for kraft mill effluents, none were available for
sulfite mill effluents.
The effect of spent sulfite liquor (SSL) on oyster larvae (Ostrea
lurida and Crassostrea gigas) and clam larvae (Tresus nutalii and
Prototheca staminea) have received considerable study. These
animals are quite sensitive to SSL compared with salmonids (Stein
et al. 1959; Woelke 1960, 1965, 1976; Woelke et al. 1970, 1972;
Cardwell et al. 1977; Cardwell and Woelke 1979) and are addressed
in more detail under receiving water bioassays. Concentrations
above 55 mg/1 (PBI) inhibit spawning; however, lower concentra-
tions can stimulate spawning, but the resulting larvae show a
higher percentage of abnormality.
-158-
-------
Larval Pacific oysters commonly develop abnormally within 48
hours in sulfite pulpmill effluent concentrations less than either
50 mg/1 PBI or 0.05 to 0.2 percent effluent (Washington State
Enforcement Project 1967 and Woelke 1965). Concentrations of
sulfite pulpmill effluent causing 50% abnormal development in
larvae of horse clam (Tresus capax and Tresus nutalii)native
littleneck clams (Protothaca staminea) and geoduck (Panope
generosa) are quite similar to those for oyster larvae (Schink
and Woelke 1973).
Magnesium-sulfite mill effluent was more toxic than ammonia-
sulfite mill effluent at pH 7. At high pH (>9) the ammonia-
sulfite mill effluent was more toxic indicating the toxicity of
ammonia.
Throughout this review little data has been found on the toxicity!
% t
of bleached sulfite mill effluent. Chlorine and chlorinated com-
pounds contribute the majority of toxicity in bleached kraft
wastes, and it appears that a similar relationship may be expected
for sulfite mills.
B. GROSS TOXICITY BIOASSAYS
There are numerous procedures for monitoring the toxicity of
pulpmill effluents. The gross toxicity of BSME can be measured
on whole effluent both before and after it is discharged into
the receiving body of water, or specific toxicity of individual
components may be determined provided chemical separation is
possible. Each of these procedures are discussed below in
sub-sections B.l, B.2 and B.3 respectively as they pertain to
the Georgia-Pacific mill in Bellingham.
1. In-Plant Effluent Bioassays
Georgia-Pacific has historically evaluated the effect of its
In-plant BSME on resident and migratory salmonid fish. The
-159-
-------
mill uses the Acute Toxicity Bioassay Test Method issued by DOE
in July 1974 (Johnson, personal communication). This procedure
was developed through the cooperation of Northwest Pulp and Paper
Association, National Air and Stream Improvement Council, indi-
vidual pulp and paper company representatives, Department of
Fisheries, Department of Game, and the Department of Ecology
(DOE 1974). This bioassay method (refered to, more specifically,
as the 96-hour static bioassay), entails placing the test solutions
and organisms in test chambers for a period of 96 hours.
The toxicity standards for Washington State require that 100% of
thesalmoiiid f ish tested must survive a 65% concentration of an
industry's effluent for 96 hours. All of the physical parameters
of dissolved oxygen, pH and temperature must be held within
specified tolerance limits of the test organism. Limitations
placed on test organisms include the loading density, the
size of the organism and the period of time required for accli-
mation prior to testing. The dilution water must be an
acceptable freshwater source with zero ambient toxicity. The
effluent must be stored at 4°C and bioassayed within 48 hours.
Mortality of control organisms must not exceed 5%. For more
detailed description of the bioassay procedure, see Appehdix £
Georgia-Pacific bioassay results are available for August 2, 1974,
December 13, 1977 and August 27, 1979 (Table V-3). Few bioassays
are available because prior to secondary treatment installation
in June 1979, Georgia-Pacific was required to submit the results
of only one bioassay. This requirement resulted from the fact
that Georgia-Pacific bioassays, performed prior to secondary
treatment in 1974 resulted in 100% mortality at 65% effluent
concentration. The Department of Ecology (DOE) therefore did
not require Georgia-Pacific to continue bioassays until after
secondary treatment was installed. After installation, however,
Georgia-Pacific was required to bioassay its effluent once every
2 to 3 months and submit the results biannually (Jot son,
personal communication).
-1G0-
-------
Table V-3 GEORGIA-PACIFIC BIOASSAY RESULTS
BOD
Cone.
LC20
LC50
Percent
Survival
Date
Sample
mg/1
% Volume
%
%
24-hr
48-hr
72-hr
96-hr
Aug 26,
Evaporator
3570
_
0.4
0.6
_
—
_
—
1974
condensate
Lignin products
258
-
57.0
66.0
-
-
—
-
Bleach Plant
112
—
8.0
10.0
—
—
—
Barking Plant
21
-
38.0
44.0
-
-
-
-
Untreated SME
415
-
5.2
7.7
-
-
—
-
Primary-treated SME
89
-
32
38.0
-
-
—
—
Dec 13,
Untreated SME
—
control
_
_
100
100
100
100
1977
-
control
—
-
100
100
100
100
—
5
—
-
100
100
100
100
—
5
—
-
100
100
100
100
—
10
—
-
100
100
100
100
—
10
—
-
100
100
100
100
—
18
—
-
100
100
100
100
—
18
—
-
100
100
100
100
—
32
—
-
100
100
100
100
—
32
—
—
80
80
80
80
—
65
—
-
20
20
0
0
—
65
— ¦
—
0
0
0
0
—
65
—
42
0
0
0
0
Primary-treated SME
control
100
100
100
100
—
control
—
-
100
100
100
100
—
18
—
-
100
100
100
100
-
18
—
—
100
100
100
100
-»
40
—
-
100
100
100
100
—
40
— ¦
-
100
100
100
100
—
65
—
—
100
100
100
100
65
—
-
100
100
100
100
—
65
—
-
100
100
100
100
—
100
—
-
0
0
0
0
-
100
-
-
0
0
0
0
—
—
-T"
83
™¦
Continued
-------
Table V-3, Page 2
BOD
Cone.
LC20
LC50
Percent
Survival
Date
Sample
mg/1
% volume
%
%
24 -hr
48-hr
72-hr
96-hr
Aug 27,
Secondary-treated SME
—•
control
—
—
100
100
100
100
1979
—
control
—
—
100
100
100
100
—
65
—
-
100
100
100
100
—
65
—
—
100
100
100
100
—
65
—
—
100
100
100
100
Cone. = Concentration
Sources: Dahlgren, letter of August 26, 1974
Seim, letter of December 23, 1977
Bradley, letter of September 7, 1979
o»
to
I
-------
Although only one bioassay was required, Georgia-Pacific submitted
two assay results prior to secondary treatment (August 24, 1974
and December 13, 1977) (Table V-3). In the August 1974 bioassay,
six effluent types were assayed for which LC50 values were
reported. It is apparent that the evaporator condensate and the
bleached plant effluent are.the major toxic components in the
untreated SME.
Of major interest* however, is the difference in the LC50 values
reported for untreated and primary treated SME. Primary treat-
ment reduced the toxicity from an LC50 at 7.7% effluent to one at
38%. Similar toxicity reductions occurred in the December 1977
bioassay (Table VI-3). In that test, the LC50 value of 42% for
untreated effluent was increased to 83% after primary treatment.
The juxaposition of these rather different test results shows a
45% increase in the LC50 concentration, indicating either
toxicity reductions between the 1974 and 1977 tests, or large
variabilities in effluents or test methods.
After the installation of secondary treatment in June 1979, a
bioassay was performed on August 27, 1979 as required by DOE
(Table V-3). The bioassay results do not include an LC50
value; however, there were no mortalities in 65% effluent.
Unfortunately, a bioassay was not conducted on a sample of 100%
effluent; therefore, it is not possible to determine if secondary
treatment further reduced the toxicity of primary treated
effluent.
2. Agency Fish Bioassay Studies
Investigations on the effects of SSL on fish were performed by
Williams et al.(1953),Holland et al.(1954),Lasater (1955), Lemier
(1962), and USD! (1967). The later two studies were conducted
in Bellingham Bay receiving waters.
Williams et al. (1953) studied the effects of several SSL con-
centrations on pink, chum, coho, and Chinook salmon in the
-163-
-------
laboratory. The SSL was obtained from Coos Bay Pulp Company
in Anacortes, Washington. The salmon were placed in aquaria and
exposed to SSL concentrations ranging from 50 - 5000 ppm. Exposure
periods were 13- 72 hours in duration. Williams concluded that
chinook were more susceptable to SSL than were chum or pink
salmon (Table V-4) . Death resulted in all species at concentra-
tions above 2700 ppm.
Williams et al.(1953) also found that although some concentra-
tions of SSL were not lethal, noticeable deleterious effects
(equilibrium loss, sluggish behavior, and reduced feeding) were
produced in many cases. He felt this factor was important since
experience has shown that fish, not given an adequate start in
life, are subject to a higher mortality in their early life
history.
Williams further concluded that older salmon were more tolerant^
to SSL. He conducted numerous tests on a wide range of age
groups, but only two were actually exposed under identical
conditions; therefore, his above conclusion would only be valid
for these two age groups (Table V-5). The small range of toler-
ance limits reported reduce the significance of William's
conclusion (above).
Holland et al. (1954) also addressed the question of SSL tolerance
on various age groups of salmon. His conclusions were somewhat
contrary to those of Williams et al. (1953). Holland concluded
that older salmon were less tolerant of SSL (Table V-6). Holland
exposed several age groups of chinook, chum, pink and coho
salmon to concentrations of Ca-based SSL for 23 -30 days. The
"apparent tolerance levels" in ppm SSL were determined for each
age group (Table V-6) . The reisults do appear to show that older
salmon have a lower tolerance to SSL, but the experiments
lacked uniformity. The exposure medium varied greatly in salinity.
This variation in medium may influence the tolerance limits
-164-
-------
Table V-4 MAXIMUM TOLERANCE LIMITS* (ppm SSL) FOR 190 DAY OLD
' CHINOOK, CHUM AND PINK SALMON EXPOSED FOR 72 HOURS
Source: Williams et al. 1953
Species Maximum Tolerance Limits
Chinook between 933 and 1727
Chum between 1000 and 1937
Pink between 1877 and 2673
*
Tolerance limit (SSL concentration (ppm) that produces
approximately a 5% kill).
Table V-5 MAXIMUM TOLERANCE LIMITS (ppm SSL) FOR TWO AGE
GROUPS OF CHINOOK SALMON EXPOSED FOR 72 HOURS
Source: Williams et al. 1953
Maximum Tolerance
Age
Limit (ppm SSL)
190
days
993 - 1727
265
days
935 - 1997
-165-
-------
Table V-6 APPARENT TOLERANCE LEVELS IN PPM SSL FOR SEVERAL AGE
GROUPS OF CHINOOK, CHUM, PINK AND COHO SALMON
Source: Holland et al. 1954
Salmon
Test Animals
Age
(Days)
Medium
Days
Exposed
Apparent
Tolerance
Level
(ppm)
Chinook
38
2-a
30
1175
146
1-a
28
480
280
3-a
28
600
305
3-a
30
575
Chum
20
3-a
30
880
Pink
102
3-a
23
1550
198
1-a
28
530
Coho
180 (?)
2-a
30
1400
351
2-a
30
1225
412
3-a
30
1000
Key to Medium:
1 seawater
2 freshwater
3 50 - 60% seawater
a flowing water
-166-
-------
reported, for saltwater is a strong buffering, agent and may mask
the toxicity of the SSL.
An investigation by Lasater (1955) addressed the problem of SSL
toxicity and the ability of coho salmon to detect and avoid
harmful concentrations of the pulp effluent. YOung coho sal-
mon (299 to 307 days old) were placed in an aversion trough where
they could choose between clean seawater and seawater polluted
with 510 and 1060 ppm SSL. From observing the fish behavior,
Lasater concluded that although young coho salmon exhibited a
degree of aversion to SSL in seawater, it was not great enough to
protect 95% or more of the stocks from concentrations below 1060
ppm SSL. Previous studies revealed that young salmon must avoid
a concentration of 500 ppm SSL if they are to avoid SSL poisoning.
These observations of aversion behavior can be related to the
maximum surface SSL levels in Bellingham Bay observed prior to
the installation of primary treatment (Figures V-2 and v-3 ).
During the period from 1956 - 1964, SSL levels within a two mile
radius of Georgia-Pacific ranged between 25 and 6790 ppm.
Therefore, SSL levels (500 - 1060 ppm) which may be harmful, yet
undetectable for coho salmon have existed in Bellingham Bay.
LeMier (1962) conducted a one-month study to investigate the
possibilities of fish losses in Bellingham Bay due to sulfite
pulpmill wastes. The project entailed holding Chinook salmon
fry in four live-boxes, three located inside Bellingham Bay and
one control near Gooseberry Point (Figure V-4). Water samples
were analyzed bi-weekly for sulfite mill wastes, dissolved oxygen,
water temperature and chlorinity (Table V-7). Chinook salmon
at Stations I, III and IV suffered no mortality during the 30-day
exposure period. Each Of the four lots of chinook placed in
Station II, however, died within 24 hours. Station II was devoid
of oxygen and had a significantly high concentration of SSL.
Further investigations have been conducted on the high Belling-
ham Bay SSL levels recorded by federal agencies in 1959 - 1961 and
-167-
-------
Strait of
Georgia
Settlneham
Porta?*
Portals
*
San Juan
Islands
100 200
50 150 300
thousands of fMt
Figure V-2 MAXIMUM OBSERVATIONS OF SURFACE SSL IN THE
BELLINGHAM STUDY AREA
Source: USDI 1967
-168-
-------
tSeiftngham
1420
37^
129
34
870
76 —
&V/r
\y//
/' \
4 1120
' TIT
Bellingham
Bay
i«/62
V
"¦-70
4290 J?/
J?'/**-
/ X 4690,
S /-S222. T\
/ / 40
/ /
^ 4920
47-^"*
% ~.
-GwgtofPacfflc , i
** \
0 200 400
750 yards
100 300 500
Figure V-3
MAXIMUM AND MINIMUM OBSERVATIONS OF SSL IN
BELLINGHAM HARBOR DURING MAY 26 - 29, 1964.
Source: USDI 1967
-169-
-------
0 1000 2000
4000
500 1500 3000 yards
bumml
Indian
Reservation
Bellingham
1*
Bellingham Ice m
& Cold Storage
Gooseberry
Pointy control
Portage
Lummi E*L
Bellingham
Bay
5*
Point
Frances
Burk-Nefco Float
(Bellingham Mill)
Pacific American
Fisheries Float
Post
7* Point
Chuckanut
Bay
Pleasant
Governors f\ say
Point
Figure V-4 LIVE-BOX LOCATIONS IN BELLINGHAM BAY, MAY - JUNE 1962
Source: LeMier 1962 (Arabic Numerals denote hydro-
graphic stations of 1957 survey by WDF)
-170-
-------
Table V-7 SUMMARY OF DATA PERTAINING TO BELLINGHAM BAY POLLUTION STUDY, MAY - JUNE 1962
Source: LeMier 1962 See Figure V-4
Station Number
II
III
IV
TEST ANIMALS
Species
Stock
Age (days reared) at planting
Average weight
Fish-per-pound
Number per live-box
Date stocked
Mortalities
Exposure (days)
F. Chinook
Deschutes
75
14.8
307
50
May 15
0
30
F. Chinook
Deschutes
75 - 91
14.8
307
50 - 55
May 15, 19, 26
June 2, 1962
100% each
1-3
F. Chinook
Deschutes
75
14.8
307
50
May 15
0
30
F. Chinook
Deschutes
75
14.8
307
50
May 15
0
30
PHYSICAL DATA OF SAMPLES TAKEN AT SURFACE DEPTH
SSL (mean)
SSL (range)
Chlorinity (o/oo) mean
Chlorinity (o/oo) range
Dissolved Oxygen (ppm) mean
Dissolved Oxygen (ppm) range
Hater Temperature (°F) mean
Valid samples obtained
192.2 ppm
20 - 504 ppm
11.9
4.2 - 17.5
6.3
6.6 - 10.1
53.7
4
3307 ppm
1992 - 5802 ppm
9.4
7.1 - 13.1
0.0
0.0
56
4
165.7 ppm
63 - 335 ppm
7.8
4.3 - 12.4
7.4
4.7 - 8.2
56.3
.4
19.7 ppm
6 - 49 ppm
16.4
14.8 - 18.0
9.3
8.3 - 10.5
51.7
4
-------
their effect on salmon and English sole eggs (USDI 1967). The
salmon studies were conducted in June 1963 -May 1964 and May and
June 1965.
The 1963 -1964 investigations were in situ studies to delineate
areais where significant juvenile mortalities could occur. On
eleven dates, live boxes were placed at selected stations
(Figure V-5) for exposure periods of 4 to 24 hours. Periodically,
fish mortalities were observed and water samples were collected.
The 1965 investigation was a modified in situ study to examine
water quality changes associated with juvenile mortalities
(see Figure V-5 for station locations). Exposure tests were
conducted in two flow-through chambers on-board a boat. The
surface 3 feet of water at the station was pumped into each tank.
Chum salmon were exposed to the water sample for up to 4 hours.
Their behavior and mortalities were observed throughout the
exposure period.
The results of the 1953 - 1964 study, describe Area B as a zone
where conditions were frequently acutely toxic to juvenile
salmon (USDI 1967). No mortalities occurred in control Area A,
and frequent, but usually low, percentage kills occurred in
Area C.
Because of the frequent water sampling, the 1965 bioassay study
was better designed to reveal levels of water quality associated
with mortality. Results of this study are summarized in Table
V-8. Absence of mortalities at control station A are associated
with water quality values showing little influence of mill
wastes; i.e., low SSL concentrations, 00 concentrations near
saturation, normal pH, and low NH3-N concentrations. One hundred
percent kills in Area B, however, are associated with high con-
centrations of SSL, low concentrations of DO, reduced pH and
variable concentrations of NH3-N. Area B also has areas of
zero percent mortality, showing that the area is not uniformly
-172-
-------
<3»orgl^PacJHc - |
AREA
Bellingham
Bay
AREA
0 200 400 750 yards
100 300 500
Figure V-5 JUVENILE SALMON BIOASSAY STATIONS IN BELLINGHAM
BAY, 1963 - 1964 and 1965 Studies
Source: USOI 1967
-173-
-------
Table V-8 PERCENT MORTALITIES AT TERMINATION OP TESTS AND SUMMARY OF WATER QUALITY DATA, 1965
BIOASSAY STUDY IN BELLINGHAM HARBOR. Source: USDI 1967
Exposure
SSL
DO
pH
Salinity
Temp.
Test
Sta-
Mort.
Time
(ppm)
(mg/1)
(mg/1)
(o/oo)
(°C)
Cham-
Date
tion
«
(hrs) (mins)
Max.
Med.
Min.
Med.
Max.
Med.
Max.
Med.
Med.
Med.
ber
5/14
B
100
3
15
4470
3470
3.3
3.8
5.9
6.2
0.43
0.17
10.97
15.0
1
B
100
2
42
7800
3810
3.3
4.4
5.9
6.3
0.49
0.08
12.80
15.2
2
B
100
1
05
3560
3090
2.7
3.3
6.0
6.3
0.25
0.24
10.80
15.0
3
B
100
0
35
3860
3655
2.8
3.1
6.2
6.2
0.25
0.24
11.53
16.1
3
B
100
2
10
3720
3520
2.6
3.0
6.1
6.1
0.36
0.09
8.18
14.8
3
B
100
3
35
3910
3350
2.0
4.8
6.1
6.2
0.08
:
8.65
14.0
3
5/15
B
100
0
10
3760
3710
0.7
0.8
6.0
6.0
0.23
8.93
—
1
B
100
0
08
1550
—
-
-
-
-
—
—
1
B
100
0
08
1550
-
-
-
-•
0.27
—
—
1
B
100
0
06
3270
—
-
-
-
-
0.38
—
1
B
100
1
42
3920
2360
1.0
3.6
6.3
6.6
0.39
0.34
16.68
14.0
2
B
100
0
40
5040
4060
2.2
2.8
5.3
5.7
0.46
0.40
10.99
14.7
2
6/02
B
100
1
45
8240
7410
4.3
5.9
4.2
4.4
1.11
1.02
3.58
19.0
1
B
100
2
07
7870
2750
1.6
2.6
4.7
6.1
0.79
0.53
6.35
17.0
2
6/03
B
100
0
33
1790
1685
1.5
1.6
6.5
6.5
0.40
0.38
9.62
16.1
2
B
100
0
15
1490
1470
1.4
1.6
6.4
6.5
0.34
0.29
9.30
16.5
2
B
100
0
15
2080
1730
1.1
1.6
6.4
6.5
0.34
0.25
8.25
17.0
1
5/14
B
0
3
10
6820
2495
4.5
5.1
5.8
6.6
—
—
12.50
14.1
3
5/17
B
0
4
15
2380
1155
2.9
4.3
6.0
6.8
0.16
0.13
19.52
12.0
1
B
0
4
00
2150
1670
4.5
5.8
6.1
6.4
0.34
0.28
10.50
11.8
2
5/14-
1 C
A
0
29
25
123
84
8.0
8.6
7.3
7.5
0.08
0.025
6.69
13.2
4
5/15
A
0
4
45
123
101
8.0
8.2
7.3
7.3
0.08
—
8.34
12.9
4
5/16-
1 M
A
0
22
05
130
108
8.1
9.4
7.3
7.5
—
™ 'Mi
8.82
10.8
5
17
5/17-
A
0
46
45
123
60
7.6
7.8
7.6
7.9
—
24.96
12.2
4
19
6/02-
A
0
18
05
107
102
5.4
6.7
7.1
7.2
0.09
0.05
12.00
15.9
2
03
Test Chamber Key:
1 Live tank - Streeter 3 Satellite live box 5 Lupi^Jg^bpx - Streeter
2 Lucite tank - Streeter 4 Live box
-------
toxic. Zones of polluted water are present in Area B and are
moved throughout the harbor by the actions of winds and tides.
The USDI (1967) concluded that the following water quality cri-
teria must be met at all times at all points in Bellingham
Harbor if survival and well being of migrating Nooksack River and
Squalicum Creek juvenile salmon are to be assumed:
SWL less than 1000 ppm
DO greater than 5 mg/1
pH greater than 6.5
NH3-N less than 0.2 mg/1
These levels are based on the results in Table V-8.
IV and VIII discuss current water quality levels of
meters in detail.
The objectives of the English sole egg study conducted by the
USDI (1967) were to determine:
• the distribution and abundance of eggs in
Bellingham Bay and the associated water quality, and
• the relationship between the injury caused and
the strength of the dispersed SME.
The egg bioassay study wais conducted during the period of January -
April 1965 and the egg distribution study took place from January -
March 1966. For the egg distribution study, English sole eggs
were fertilized in the laboratory and then incubated for about
seven days in dilutions of SSL ranging in strength from 6-1000
ppm. Composite samples of SSL were supplied by the Scott Paper
Company from their Anacortes mill. All samples bioassayed were
at least 48 hours old. After incubation, the eggs and larvae
(yolk-sac fry) were examined under a microscope to determine
response (either injury or retarded development) to the various
concentrations of SSL. Egg distribution was determined by collecting
eggs at ten stations in northern Bellingham Bay at depths of 1,
*
17 and 33 feet {see Figure VI-5). Salinity and SSL were determined
at each site (see Table Vl-4).
Chapters
these para-
-175-
-------
The USDI (1967) found that large numbers of English sole eggs
were spawned into areas polluted by SSL (see Table .VI-41 and that
they develop in the surface layers where the highest concentra-
tions of SSL occur. The bioassay results showed that deleterious
effects occurred at concentrations of SSL chronically present
in surface waters of Bellingham Bay (Figure V-6). Significant
changes in response were rarely seen at waste concentrations of
6 ppm SSL but always at 14 ppm (Table V- 9 ), suggesting
strongly that a critical threshold existed somewhere around 10
ppm SSL. The damage induced at this threshold was not signifi-
cantly increased by augmented concentrations of SSL until another
critical level was reached at approximately 180 ppm SSL. Above
this concentration, survival of exposed eggs did not occur.
3. Oyster Larvae Receiving Water Bioassays
A widely used organism for receiving water bioassays of the maririe
waters of Washington State is the larvae of the Pacific oyster
(Crassostrea gigas) (Cardwell and Woelke 1979). The Pacific
oyster was chosen because the species is commercially important,
sensitive to low concentrations of pulpmill effluents (Gunter
and McKee I960, Woelke 1960) and amenable to standard testing in
the laboratory (Woelke et al. 1972). The method of testing involves
measuring in the laboratory the effects of samples of natural
development from the fertilized egg to the fully-shelled 48-hour-
old veliger. The bioassays sure referenced to the following
selected water-quality parameters: Pearl Benson Index (PBI)
salinity and age of the seawater sample at the time testing
commenced. A review of the specific procedures and considera-
tions of the oyster larvae bioassay is contained in Appendix
E.
A general indication of the receiving water biomonitoring
responses for northern Puget Sound (Anacortes to Bellingham)
has been presented for the period 1961 -1976 by Cardwell and
Woelke (1979). Additional unpublished data for 1977 and 1978
-176-
-------
Percent of eggs killed during
incubation.
Percent of eggs which failed
to hatch within normal incubation
period.
m
o
(9
Ui
a
<
u
Q
X
(-
<
z
o
t-
o
u
mJ
<
u.
z
o
X
5
(/>
o
(9
IU
50-
40 -
30-
20-
10-
0
I
100-
90-
8 0-
70-
60-
50-
40-
30-
20-
10-
0 -
.• •_
£.2.0. ULPJr.
i >iiii i
5.6 13.5 32 78 180 420 1000
P B I (ppm)
l i I l I I l l
f 5.6 13.5 32 75 180 420 000
P B I (ppm)
Percent of eggs which failed to
develop into normal fry within
normal incubation period.
a.
o
-j
Ui
>
UI
O'
3^
< 2
«• IE
1®
z
in ~
(9
o
Ui
100-
90-
80-
70-
60-
50-
40-
30-
20-
10-
0-
y
-4
9
y
C 0 N T R 0 L
I I I I I I l I
1 5.6 13.5 32 75 180 420 1000
P BI (ppm)
Figure V-6 THREE RESPONSES OF FERTILIZED ENGLISH SOLE EGGS TO VARIOUS
CONCENTRATIONS OF SULFITE WASTE LIQUOR.
Source: USDI 1967
-177-
-------
Table'V-9. INCREASE IN RESPONSE OF ENGLISH SOLE EGGS TO
INCREASING CONCENTRATIONS OF SULFITE WASTE LIQUOR
Source: USDI 1967
SWL
(ppm)
Dead Eggs
(%)
Faily
to Hatch
(%)
Fail to Become
Normal Larvae
(%)
6
14
15
29
14
509
215
65
32
659
288
73
75
805
358
78
180
836
369
126
420
709
931
228
1,000
1,150
1
,631
239
-178-
-------
were supplied by Cardwell. Bioassay of samples of marine
receiving water taken in the vicinity of major freshwater sources
may have an additive interaction (Cardwell et al. 1979) with
toxic effluents when salinity falls below 20 ppt determined by
Woelke (1968). These data are analyzed with and without
screening to remove those responses obtained at salinities below
20 ppt.
The Washington Department of Fisheries. (WDF) Marine Water Quality
Compendium data (Cardwell and Woelke 1979) for the period from
1961 to 1978 are summarized and compared for the periods before
and after primary treatment of the effluents from the Georgia-
Pacific pulpmill in Bellingham (Table V-10). Since the Nooksack
River discharges into the western portion of Bellingham Bay,
surface and nearshore salinities are frequently less than 20 ppt.
Bleached sulfite mill effluent is discharged in low-salinity
marine water along the east shore of the Bay. The data in the
WDF Compendium have been screened to remove all responses from
receiving water samples with a salinity of 19.99 ppt or less
(Woelke 1972). The screening of the data reduced the interactive
effect of low salinity, but also removed most responses at the
highest PBI concentrations, particularly those nearest the
effluent discharge point.
The toxicity stations analyzed are shown in Figure V-7 . Analyses
of the data, including statistical manipulation and relationship
to currents and water quality are presented in Chapter VIII.
C. MAJOR EFFLUENT COMPOUNDS AND ORGANISM RESPONSE
1. Introduction
Isolating the individual constituents of BSME and determining
their toxic nature is valuable in the sense that a general
179-
-------
Table V-10
Comparison of WDF Compendium Data (Cardwell and Hoelke 1979) by station, mean percent abnormal response and mean
FBI concentration for depths 0-3 ¦ and > 4 n for the period 1961-72 and 1973-78. Data from samples with salinities
of 19.99 ppt or less were removed.
Number
(0-3m)
Mean
<0-3a)
Mean
(>4m)
Mean
of
1961-72
Standard
FBI
1973-78
FBI
1973-78
FBI
Station
samples
Mean Z
deviation
conc.
Mean X
conc.
Mean Z
conc.
number
n
abnormal
SD
(pp«)
n
abnormal
SD
(PP»>
n
abnormal
SD
(ppm)
1-1115
14
97.60
.0893
515.43
18
99.77
.0068
98.78
1-1417
12
99.80
.0084
475.25
19
45.00
.4656
78.32
16
7.40
.2488
5.13
1-1620
12
76.10
.4325
74.00
22
12.90
.2979
46.36
22
0.04
.0208
2.64
1-2307
3
66.70
.5774
364.00
1-2217
30
32.60
.3929
31.10
22
26.40
.3732
12.02
12
8.4
.2885
1.00
1-1331
9
84.80
.1953
133.33
6
15.30
.0796
17.33
2
9.25
.0346
7.00
1-2417
3
2.00
8
50.01
.5344
18.75
1-3013
33
2.90
.0751
8.27
28
0.13
.0023
1.07
14
0.08
.0017
0.43
1-2524
3
1.00
.0165
8.00
8
0i90
.0104
11.00
1-3916
3
95.67
.0401
47.00
2
0.60
.0028
5.00
1-3308
33
2.00
.0459
6.00
10
0.20
.0035
1.00
1-2731
24
28.20
.4272
24.63
27
9.70
.2799
8.07
16
0.16
.0052
2.25
1-1644
39
23.56
.4193
19.27
14
1.00
.0186
3.00
24
0.13
.0020
1.92
1-3505
10
0.20
.0053
0.60
1-411S
27
0.83
.0200
2.00
8
1.00
.0116
4.75
1-2134
3
3.20
.0353
11.00
8
0.90
.0165
4.00
1-3926
36
9.30
.2469
9.54
28
1.40
.0331
1.14
12
0.15
.0022
0.50
1-3236
30
14.10
.3018
12.20
12
1.00
.0204
3.83
1-0071
9
1.20
.0113
0.67
14
0.60
.0060
2.00
24
0.22
.0040
0.58
1-4035
21
0.70
.0129
3.86
6
0.30
.0065
1.00
1-4629
30
0.90
.0201
4.70
10
20.40
.4195
14.20
1-5715
30
1.20
.0274
1.80
10
0.20
.0034
0.60
1-2650
3
4.10
.0352
1.00
10
0.20
.0041
1.20
1-5232
3
0.50
.0087
2.00
10
0.60
.0081
0.80
1-5515
27
2.40
.0471
1.39
10
0.20
.0057
0.00
1-5622
27
0.04
.0011
2.22
8
0.60
.0110
1.00
1-5423
26
0.70
.0210
2.00
8
0.20
.0032
0.50
1-5331
15
2.00
.0210
1.70
10
19.00
.3905
0.40
1-5730
30
0.30
.0105
0.75
8
0.00
1-5333
21
29.70
.4549
82.71
8
0.20
.0038
0.25
1-5037
18
34.00
.4504
186.00
10
40.40
.5129
34.80
1-5246
33
8.90
.2750
5.55
10
0.60
.0065
2.00
2
0.00
.0000
1.00
E-593
£"378
£-162
-------
01*0071*
T
Strait of
Georgia
I
iMMkwk Riy«c
JqT
11-0049*
San Juan
Islands
100 200
Lummi Bay , / tbirowt
^S**/01*1331
/ •
/^l|;;sa^oi5i*
bmM
111
l01-3|j)B»
Portag*
UMttmi
01*23071
01-11115 *,
01*14lle*
01-1417 [•_
BttlMngham
Portaga 01-1620*
««« 01*2211
01-0152* •
Chuekanut Bay\
Plaaaant Bay
»ay i /-^XTS.
01-2417*
Eliza laL _ \^; Ny
Sinclair
Isl.
01*2731
•01-3236
Wildcat Co««
• 1-2524
01-3013*
Fidalgo
Vandovi
Isl.
01-3926
4035 #
S«mi»h
Isl.
01-3308*
01-2134*
7 i
i i
* t
01*3505.
01*3806*
Samiah Bay
*01-4115
1-4629
Anacortaa'
Padilla Bay
400
50 150 300
thousands of teat
Figure V-7 LOCATIONS SAMPLED IN NORTH PUGET SOUND HISTORICAL
BIOMONITORING
Source: Cardwell and Woelke 1979
-181-
-------
knowledge of which components are responsible for the toxic
characteristic of BSME can be obtained. It should be understood,
however, that the toxicity of each component is not necessarily
additive. Toxicants can exhibit synergistic or antagonistic
reactions when in the presence of other chemicals.
The toxicity of BSME components are measured using bioassay
procedures similar to those used in assaying whole BSME. The
studies presented below represent the responses of a wide
variety of aquatic life to BSME.
2. Organic Aoids and Related Compounds
Leach and Thakore (1977) determined the major toxicants of sulfite
pulpmill effluents to be the resin acids and juvabiones. Other
compounds which contribute to the toxicity include the lignin
degradation products (Walden 1976) and the chlorolignins (Leach
and Thakore 1977).
The compounds and their associated toxicities are presented in
Table V—11. Resin acids are the primary toxic components found
in softwood pulping waste streams in Canada. The individual
acids had 96-hr LC50's for coho salmon of 0.2 - 0.75 mg/1 in
static bioassays with 4-8 hour solution replacement. Tests with
juvenile rainbow trout without replacement resulted in 96-hour
LCSO's of 0.4-1.1 mg/1. A marked increase in resin acid tox-
icity occurred with decreasing pH in the range of 7.5-6.4.
The diterpene alcohols were found in trace quantities with 96-
hr LC50's ranging from 0.3-1.8 mg/1. Several naturally occurring
insect juvenile hormone mimics related to juvabione had 96-hr
LC50's ranging from 0.8-2.0 mg/1 for rainbow trout. Leach and
and Thakore (1977) found that secondary treatment reduced or
eliminated the toxicity of most of these chemicals; however,
some do not readily degrade and remain toxic. It should be noted
-182-
-------
TABLE V-ll MAJOR COMPOUNDS IDENTIFIED IN SULFITE PULPING OPERATIONS WHICH ARE TOXIC
TO FISH AND INVERTEBRATES
Fraction
Chemical
Species
Tested
Species
size (g)
96-hr
LC50
(mg/i)
Sublethal Response
of
96-hr
LC50
Resin Acids
Abietic
Coho
0.2-0.75
0.41
Rainbow
Juvenile
0.7
Dyhydroabietic
Coho
0.2-0.75
0.75
Rainbow
Juvenile
1.1
Isopimaric
Coho
0.2-0.75
0.22
Rainbow
Juvenile
0.4
Pimaric
Coho
0.2-0.75
0.32
Rainbow
Juvenile
0.8
Sandaracopimaric
Coho
0.2-0.75
0.36
Oeterpene Alcohols
Pimarol
Rainbow
Juvenile
0.3
Isopimarol
••
N
0.3
Dehydroabietol
m
N
0.8
Abietol
m
m
1.8
Juvabiones
juvabione
Rainbow
Juvenile
1.5
Juvabiol
m
N
1.8
A1*1 -Dehydro j uvabiona
m
m
0.8
Dehydrojuvabione
m
¦
2.0
Lonq-Chain Fatty Acids
Oehydroabietic acid (RA)
Sockeye
20
Metabolism -
inability of SW acclimated smolts
0.65 mg/1
to adapt to F.H.
Sockeye
20
Morphology -
FW acclimated smolts:
0.65 mg/1
edema, bloating of gut
Sockeye
N.D.
Morphology -
SW acclimated smolts<
0.65 mg/1
loss of water from muscle tissue
Sockeye
N.D.
Metabolism -
high accumulation in viscera (|ig/g)
0.65 mg/1
brain<*619.8.
Jcidney»278.1, liver»262.5
Rainbow
N.D.
Metabolism -
high accumulation in viscera (|ig/g)
0.65 mg/1
brain°154.3,
kidneys182.5, liver=»290.6
Estuarine
N.D.
Metabolism -
25 mg/1 accumulatiohln tissues
0.65 mg/1
Comments
Reference
CO
U>
I
Static with 4-8 hr replacement
Static without replacement
Static with 4-8 hr replacement
Static without replacement
Static with 4-8 hr replacement
Static without replacement
Static with 4-8 hr replacement
Static without replacement
Static with 4-8 hr replacement
Static without replacement
Static with 4 hr replacement
lation
amphipods
Continuous flow bioassay
Freshwater, 5 day exjposur
Continuous flow bioassay
Freshwater, 5 day exposur
Continuous flow bioassay
3
3
3
3
3
Referencesi 'Leach & Thakore 1977 2Davis 1976 3JCruzynski 1979
-------
that these tests have all been conducted in freshwater. Dis-
charge of organic pulping compounds into marine receiving waters
may result in more rapid reduction in the toxicity in the mixing
zone than occurs in freshwater.
3. Bleach and Related Compounds
Enormous quantities of pulp are bleached in the manufacture of
paper. Sulfite pulps are usually bleached by the CEH multi-
stage process (chlorination, alkaline extraction and hypochlor-
ite stages). The chlorination stage delignifies the pulp by
forming chlorolignin compounds which are subsequently removed
in the alkaline extraction stage. The pulp is then bleached or
i
brightened during the final hypochlorite stage. The bleach
waters are then discharged along with the sulfite mill effluent
into Bellingham Bay.
At the Georgia Pacific mill in Bellingham, bleach waste emanates
mainly from the sulfite process section of the plant, although
other sections do use lesser amounts of bleach (Bruce Johnson,
personal communication). Additionally, the chlor-alkali plant
discharges chlorinated wastes into Bellingham Bay.
Concern regarding the environmental effects of discharging chlor-
ine and chlorine by-products to fresh and marine waters has led
to an increase in the amount of scientific investigations in the
last 10 years. The toxicity of chlorine in freshwater has re-
ceived extensive investigation; however, it has been only recent-
ly that the problem of chloro-organics with potential health and
environmental effects has been identified. The chemistry of
chlorine in seawater has receatly been recognized as much more
complex than that in freshwater and has stimulated new research
to determine the chemical reaction rates and biological toxicity
in estuarine and marine ecosystems.
The bromide ion in seawater has been shown to play a major role
-184-
-------
in chlorine chemistry (Lewis 1966). The oxidative capacity of
chlorine is transferred to bromide ion as well as various other
by-products (e.g. chlorinated hydrocarbons, chloramines, broma-
mines, etc.). Sugara and Helz (1977) have recently proposed a
sequence of reactions for chlorine degradation in a marine envi-
ronment (Figure V-8). The actual reaction products formed dur-
ing the conversion of one oxidant into another are dependent
upon several variables, among which are pH, salinity (amount of
Br ), ammonia nitrogen, chlorine dose, and temperature (Helz et
al. 1978).
The importance of ammonia nitrogen concentration in the chemistry
of chlorinated seawater and its toxicological implications has
been examined by Inmanii and Johnson (1978) . In full-strength
chlorinated seawater bromamines may be formed from the hypo-
bromous acid resulting from bromide hydrolysis at low ammonia
nitrogen concentrations. The degree of halogen substitution
on nitrogen will be determined by pH and the halogen ammonia
ratio(Johnson and Overby 1971).
For ammonia nitrogen level less than 0.4 mg/1, pH 8.1, and suffi-
ciently large chlorine doses, tribromamine and hypobromous acid
are the major products. When the ammonia nitrogen level is
greater than 0.5 mg/1 and the chlorine dose is less than 2.5
mg/1, monochloramine competes with bromide oxidation and a halo-
amine mixture of monochloramine and dibromamine results. At
even greater ammonia concentrations and longer time, monochlor-
amine becomes the predominant oxidant species.
Inman and Johnson (1978) have also determined the critical
ammonia nitrogen:bromide ratio where monochloramine formation
begins to predominate over bromamine formation. This ratio
reduced to 0.008 at pH 8.1. At higher ratios the authors feel
that monochloramine should predominate after 30 minutes to one
hour. At lower ratios, dibromamine would be the major oxidant.
However, they point out that small amounts of monochloramine
may be present as part of the total oxidant concentration in suf-
-185-
-------
H0C1 + H+ + CI"
HOC1 | n OCl" + H+
Organics
Br
NH
>> OBr"
NH.C1, NHC1
NCI
HOBr 4
Organics
Organics
Chloro-organics
NH-Br, NHBr
NBr
Organics
Degradation to CI
Bromo-organics~
Degradation to Br
Figure V-8. PROPOSED SEQUENCE OF REACTIONS FOR THE DEGRADATION
OF CHLORINE IN AQUATIC SYSTEMS. Reactions of HOC1
and HOBr with inorganic reducing agents have been
omitted because they are probably of negligible
importance in most cases. (Taken from Sugam and
Helz 1977.)
-18 6-
-------
ficient amounts to exert a toxic effect on various forms of
marine life. At present, there is inadequate analytical method-
ology for the estimation of low concentrations (yg/l) of chlorine
and, none of the present methods is specific for chlorine or even
the halogens.
Several factors were reviewed by Crumley et al.(1980) which af-
fect the toxicity of chlorine to marine organisms. These in-
cluded concentration, exposure time, temperature, chemical spe-
cies of chlorine and biotic factors such as species, life stage
and size of organism. In addition, other environmental factors
such as pH and metal pollutants (copper and nickel) modify
toxicity; however the two factors of most importance in the de-
mination of toxicity are concentration and exposure time. These
factors have not been defined for pulp mill effluents due to
the complex nature of the effluent; however, longer exposure
times are suspected to occur rather than the relatively short
time-concentration relationships illustrated by Larson and
Schlesinger (1978) normally resulting from intermittent power
plant chlorination.
In determining the impact of chlorine on an aquatic community,
consideration must be given to the species composition of that
community. Factors such as life stage (egg, larvae, juvenile,
adult), size, and species specific sensitivity appear to influ-
ence toxicity.
Thatcher (1978) conducted a series of 96-hr LC50 continuous-
flow bioassays to determine the impact of chlorination on 15
estuarine and marine fish and invertebrates common to Puget
Sound and adjacent waters (Table V-12). A thermal stress was
included and total residual oxidant (TRO) concentrations were
measured by amperometric titration. In general, the fishes
were more sensitive them the invertebrates. Based on LC50
values, the 15 species fell into three distinct groups with
differing sensitivity to chlorinated seawater. The most sensi-
tive group included coho, pink and chinook salmon, Pacific her-
-187-
-------
Table V-12. TOXICITY OF CHLORINE TO MARINE ORGANISMS IN PUGET SOUND AND ADJACENT WATERS SELECTED FROM:
CRUMLEY, STOBER AND DINNEL I960.
Test
Organism
Test Concentra-
Conditions1 tion (ppm)2 Remarks
References
MOLLUSCA
Crassostrea CB, SW, LS
g*9aa
ARTHROPODA-
CRUSTACEA
Anonyx sp. CB, SW, LS
Crangon CB, SW, LS
nigricauda
Hemlgrapsus CB, SW, LS
nudus, H.
oreqonensjs
Neomysis sp. CB, SW, LS
Pandalus
danae
Pandalus
CB, SW, LS
CB, SW, LS
gonlurus
Pontoqenla CB, SW# LS
sp.
CLUPEIDAE- herrings
Clupea harenqua
gallasi CB, SW, LS
0.44 (Amp) 48 hr EC50; 10 day laxvae
0.14S (Amp) 96-hr LC50, 10°C acclimation temp; 14.8°C
exposure tempt salinity 18 %> ; pH 8
0.134 (Amp) 96-hr LC50; 10°C acclimation temp.; 14.8°C
exposure temp.; salinity 28 %, ; pH 8
1.418 (Amp) 96-hr LC50, 10°C acclimation temp.; 14.8°C
exposure temp.} salinity 28 %, ; pH 8
0.162 (Amp) 96-hr LC50; 10°C acclimation tenq?.; 14.8°C
exposure tempi salinity 28 %> ? pH 8
0.210 ; pH 8
0.687 (Amp) 96-hr LC50;. 10°C acclimation ten%>.; 14.8°C
exposure temp.; salinity 28 e/a> ; pH 8
96-hr LC50; 10°C acclimation temp.; 14.8°C
0.057 (An$>) exposure temp.; salinity 28 %» ; pH 8
Continued.
Thatcher et al. 1976
Thatcher 1978
Thatcher 1978
Thatcher 1978
Thatcher 1978
Thatcher et al. 1976
Thatcher 1978
Thatcher 1978
Thatcher 1978
-------
Table V-12. Page 2.
Test
Organism
Test
Conditions *
Concentra-
tion (ppm)2 Remarks
References
SALMONIDAE -
Trout and Salmon
Oncorhynchus CB, SW, LS
gorbuscha
O. gorbuscha CB, SW, LS
O. kisutch CB, SW, LS
> 0.023
< 0.052 (Amp)
0.5 (OT)
0.25
0.10
0.208 (Amp)
0.130
0.142
0.002-0.5
96-hr LC50; 10°C acclimation temp.j 14.8°C
exposure teny?.; salinity %, » PH 8
7.5 min. LC50, salinity 20 - 26 ;
pH 7.23 - 7.80
60 min LC50
60 min LC50, +9.9°C temp, shock
60 min LC50; 12.7°C, pH 7.8, salinity 29.6
60 min LC50; 12.7°C +7.3 C°temp. shock, pH 8;
salinity 28.8 %,
24-hr LC50; 12.1°C temp.; pH 7.9t salinity
29.4
avoidance, 12°C
Thatcher 1978
Stober & Hanson
1974
Stober et al. 1980.
O. kisutch CB, SW, LS
O. tshawytscha CB, SW, LS
0. tshawytscha CB, SW, LS
GASTEROSTEIDAE -
Sticklebacks
Gasterosteus CB, SW, LS
aculeatus
0.032 (Amp) 96-hr LC50; 10°C acclimation temp.; 14.8°C
> 0.038
< 0.065 (Amp)
0.5 (OT)
0.25
0.05
0.167
exposure temp.) salinity 28 /„i pH 8
96-hr LC50; 10°C acclimation tenq?.; 14.8°C
exposure teng>; salinity 28 , pH 8
15 min LC50; salinity 20-28 %, t pH 7.66-7.83
60 min LC50
60 min LC50, +10°C temp, shock
96-hr LC50; 10°C acclimation ten%>; 14.8°C
e^>osure temp.; salinity 28 °/oo » pH 8
Thatcher 1978
Thatcher 1978
Stober & Hanson 1974
Thatcher 1978
Continued.
-------
Table V-12. Page 3
Test
Organism
Test
Conditions1
Concentra-
tion (ppm)2 Remarks
References
EMBIOTOCIDAIE-
Surf perches
Cymatogaster CB, SW, LS
aggregata
C. aggretaga CB, SW, LS
AMMODYTIDAE-
Sandlances
Ammodytea
hexapterus
CB, SW, LH
PLEURONECTIDAE-
Right-eye flounders
Parophrys CB, SW, LW
vetulus
0.2 (An%>)
0.301
1.0
0.175-0.5
0.071 (Any?)
0.082 (Amp)
No mortality. 60 min. exposure.
60 min. LC50j 13°C; pH 8.1
100% mortality
avoidance ; 12°C
96-hr LC50; 10°C acclimation temp.; 14.8°C
exposure temp, t salinity 28 °/» > pH 8
96-hr LC50; 10°C acclimation temp.; 14.8°C
exposure temp.; salinity 28 ; pH 8
0.073 (Amp) 96-hr LC50; 10°C acclimation ten{>.; 14.8°C
exposure temp.; salinity 28 %> pH 8
Stober et al. 1980
Thatcher 1978
Thatcher et al. 1976
Thatcher 1978
1. SB = static bioassay, CB = constant flow bioassay, SW = saltwater, FW = freshwater, LS - lab study
FS = field study
2. Amp = amperometric titration, OT = acid orthotolodine
-------
ring, shiner perch, English sole, Pacific sand lance, and a
shrimp (Pandalus goniurus). The 96-hr LC50 values for this
group were 0.026 to 0.119 mg/1 TRO. The group of intermediate
sensitivity included the shrimp (Crangon nigricauda), the amphi-
pod (Ammyx sp.), the mysid (Neomysis sp.), the threespine stickle-
back (Gasterosteus aculeatus) and the coon stripe shrimp (Pandalus
danae). Their 96-hr LC50 values ranged from 0.118 to 0.199 mg/1.
The most resistant group consisted of the amphipod, Pontoqeneia
sp., and the shore crabs, Hemigrapsus nudus and H. oregonensls.
Their 96-hr LC50 values ranged from 0.583 to 1.530 mg/1 TRO.
Comparing two species in seawater, Stober et al. (1980) found
that coho salmon (Oncorhychus kisutch) proved to be more sensi-
tive to TRO than shiner perch (Cymatogaster aggregata) with a
24-hr LC50 of 0.123 mg/1 for shiner perch approximating a 12-hr
LC50 for coho salmon of 0.114 mg/1 (Table V-12). Coho salmon
were also significantly more sensitive to chlorinated seawater
for short exposure time of 7.5, 15, 30 and 60 minutes than
shiner perch. A three-way matrix test design with chlorine con-
centration, exposure time and temperature was used as test vari-
ables. Exposures of 60 minutes or less to shiner perch produced
no mortalities in concentrations less than 0.2 mg/1 TRO, although
increased respiration rates indicated a response to chlorinated
seawater at levels of 0.10 mg/1. TRO concentrations of more
than 1.0 mg/1 produced 100 percent mortality at exposures of 7.5
minutes or more. The shiner perch were significantly more
sensitive to chlorine with increasing exposure time (up to 60
minutes ) and a temperature shock of +7C (but not at +3C).
Coho salmon experienced no mortality below 0.10 mg/1 TRO for the
range of exposures and temperatures tested, while 100 percent
mortality was observed at concentrations greater than 0.50 mg/1
TRO. A temperature shock of +7C resulted in a significant
decline in LC50 values from exposure times of 7.5, 15 and 30 min-
utes. A +3C temperature shock above ambient had no significant
effect.
-191-
-------
In an earlier experiment using a similar type matrix design,
Stober and Hanson (1974) found pink and Chinook salmon juveniles
were also more sensitive to residual chlorine at elevated temper-
atures (Table V-12). Temperature increases of 9.9 to IOC above
acclimation and 0.5 rag/1 TRO exerted the greatest toxic effect.
Behavioral responses are some of the more important sublethal
effects which can be used to demonstrate ecological impacts of
chlorinated effluents. If organisms are attracted to plumes of
chlorinated water, the toxic effects in the field could approxi-
mate those seen in an acute bioassay. However, if organisms
avoid a chlorinated plume, toxicity may be minimal, but the
mixing zone must then be considered an uninhabitable area for
those organisms showing avoidance and the ecological impacts
assessed in a different manner. The behavioral responses
(avoidance or attraction) become important when considering the
ecological impact on individual species.
Stober et al.(1980) determined the behavioral response of coho
salmon and shiner perch to chlorinated and heated seawater.
A significant avoidance threshold for coho occurred at 2 yg/1
TRO and was reinforced with increased temperature. Shiner perch
avoided TRO at 175 yg/1, while a significant preference res-
ponse at 16C and 20C occurred at 10, 25 and 50 and 100 yg/1.
Thatcher (1978) determined that the 96-hr LC50 for shiner perch
in chlorinated seawater was 71 yg/1 TRO and consequently,
continuous discharges of heated seawater having a chlorine TRO
of 71-100 yg/1 could attract shiner perch and eventually result
in adverse sublethal effects.
Georgia-Pacific has reported average residual chlorine concen-
tractions in their discharge in 1966, 1967, 1976, 1977, 1978 and
1979 of 3.8, 3.3, 0.94, 0.9, 0.68 and 0.55 ppm, respectively.
Based on the most recent information presented above, chlorine-
related effects may have occurred in the mixing zone either due
to toxicological effects on non-motile or behavioral modifications
of motile organisms. Outside the mixing zone the ecological
-192-
-------
effects of long-term exposures of marine life to total residual
oxidant and persistent chlorination by-products are unknown.
-193-
-------
REFERENCES
Bradley, D. September 7, 1979. Letter to Warren Mowry, Envir-
onmental Control Director, Georgia-Pacific Corporation.
Cardwell, R.D. and C.E. Woelke. 1979. Marine Water Quality
Compendium for Washington State. VoI7~I and II. Washington
State Department of Fisheries.
Cardwell, R.D., C;E. Woelke, M.I. Carr, and E.W, Sanborn. 1977.
"Evaluation of the Efficacy of Sulfite Pulpmill" IN: Mayer,
F.L. and Hamelink (eds.), Aquatic Toxicology and Hazard
Evaluation. Am. Soc. Test. Mater. Spec. Tech. Publi 634,
Philadelphia, PA.
Cardwell, R.D., Charles E. Woelke, Mark I Carr, and E.W. Sanborn.
April 1979. Toxic Substance and Watet Quality Effects on
Larval Marine Organisms"! Washington State Department of
Fisheries Technical Report No. 45.
Crumley, S.C, Q.J. Stober, and P.A. Dinnel. 1980. Evaluation
of Factors Affecting the Toxicity of Chlorine to Aquatic
Organisms. Prepared for U.S. Nuclear Reg. Commission^
Contract No. NRC-04-75-222.
Dahlgren, E. Letter of August 26, 1974.
Davis, John C. 1976. "Progression Sublethal Effect Studies with
Kraft Pulpmill Effluent and Salmonids? J. Fish Res. Board
of Canada 33:2031-2035.
Gazdziauskaite, I.B. 1971a. "Effects of Effluents from the Sov-
etsk and Neman mills on the biology of Pontogammarus robust-
oides. (1) Vitality. (2) Respiration Intensity'.' Liet. TSR
Mokslu. Adad. Darbai Ser. C. Nc. 2:93. (Ab. Bull. Paper
Chemistry 43:10694).
Gazdziauskaite, I.B. 1971b. "Effect of Effluents from the
Sovetsk and Neman Sulfite Pulp Mills on the Fertility of
Pontogammarus robustoides (Grimm) sars? Rybokhoz. Isuch.
Vnutr. Vodoemov No. 6:29-31. (Ab. Bull. Inst. Paper Chem
43:3025). —
Gunter, G. and J.W. McKee. 1960. On Oysters and Sulfite Waste
Liquor. Washington Pollution Control Commission. Olympia,
Washington. 93 pp.
Helz, G.R., R. Sugam and R.Y. Hsu. 1978. "Chlorine Degradation
and Halocarbon Production in Estuarine Waters." IN: Water
Chlorination: Environmental Impact and Health Effects.
R.J. Jolley, H. Gorchev and D.H. Hamilton (eds.). Ann Arbor
Science Vol. I. pp 209-222.
-194-
-------
Holland, G.A., J.E. Lasater, W.E. Eldridge, E.D. Neumann.
January 27, 1954. Resume of the Effects of Industrial
Pollution on Salmon and its Natural Foods. Deception Pass
Marine Research Station. State Dept. of Fisheries.
Hutchins, F.E. 1979. Toxicity of Pulp_and Papermill Effluents
A Literature Review. EPA-600/3-79-013. pp. 44.
Inman, G.W. and D. Johnson. 1978. "The Effect of Ammonia
Concentration on the Chemistry of Chlorinated Sea Water."
IN: Water Chlorination: Environmental impact and Health
Effects. R.J. Jolley, H. Gorchev and D.H. Hamilton (eds.).
Ann Arbor Science. . Vol I, pp. 235-252.
Johnson, Bruce. January 16, 1980. Personal communication to
Kathy Pazera, Biologist, Northwest Environmental Consultants,
Inc.
Johnson, J.D. and R. Overby. 1971. "Bromine and Broamine Disin-
fection Chemistry." J. San. Eng. Div. Am. Soc. Civ. Eng.
97:617-628. ——
Kruzynski, G.M. 1979. Uptake and Distribution of Dehydroabietic;
Acid in Sockeye Salmon Smolts and Mature Rainbow Trout.
Unpublished paper submitted to Journal of Fish. Res. Board
of Canada.
Larson, G.L. and D.A. Schlesinger. 1978. "Toward an Understand-
ing of the Toxicity of Intermittent Exposures of Total
Residual Chlorine to Freshwater Fishes." IN: Water Chlorin-
ation: Environmental Impact and Health Effects. R.J. Jolley,
H. Gorchev, and D.H. Hamilton (eds.). Ann Arbor Science
Vol. 2, pp. 111-122.
Lasater, J.E. March 1955. Preliminary Studies on the Aversion
of Young Silver Salmon to Pulpmill Wastes. Deception Pass
Marine Research Station. State of Washington Dept. of
Fisheries. 16 pp.
Leach, J.M. and A.N. Thakore. 1977. "Compounds Toxic to Fish
in Pulpmill Waste Streams." Prog. Water. Tech. Vol. 9
pp. 787-798.
Lemier, E.H. 1962. Bellingham Bay Water Quality Study, May -
June, 1962. State of Washington Dept. of Fisheries.
Lewis, B.G. 1966. "Chlorination and Mussel Control. I. The
Chemistry of Chlorinated Sea Water: A Review of the Liter-
ature." Central Electricity Research Labs. 13 pp.
-195-
-------
Rosehart, R.G., G.W. Osborn, and R. Mettinen. 1974. "Origins of
Toxicity in Sulfite Pulping." Pulp and Paper Mag. Canada
75:63..
Schink, T.D. and C.E. Woelke. 1973. Development of an In-Situ
Marine Bioassay with Clams. Pinal Report for Grant 18050DOJ
to U.S. EPA, Naragannsett, RI.
Seim, . Letter of December 23, 1977.
Seppovaara, 0. 1973. "The Toxicity of the Sulfate Pulp Bleaching
Effluents." Paperi Ja Puu.55:713. (Ab. Bull. Inst. Paper
Chem. 44:109IUTI !
Seppovaara, 0. and P. Hynninen. 1970. "On the Toxicity of Sulfate
Mill Condensates." Paperi ja Puu. 52:11 (Ab. Bull. Inst.
Paper Chem. 41:487).
Sprague, J.B. 1971. "Measurements of Pollutant Toxicity to
Fish, III. Sublethal Effects and "safe" Concentrations."
Water Res. 5(6):245-266.
Stein, J.E., R.E. Petersen, J.G. Denison, G.M. Clark, I.E. Ellisi
1959. The Spawning of Olympic Oysters (Ostrea lurida)
Kept in'Spent Sulfite Liquor (SSL). Olympia Research Division
Report, Rayonier, Inc., Shelton, WA.
Stober, Q.J. and C.H. Hanson. 1974. "Toxicity of Chlorine and
Heat to Pink (Oncorhynchus gorbuscha) and Chinook Salmon
(0., tshawytscha)." Trans. Am. Fish. Soc. 103:569.
Stober, Q.J., P.A. Dinnel, E.F. Hurlburt, and D.H. DiJulio. 1980.
"Acute Toxicity and Behavioral Responses of Coho Salmon
(Oncorhynchus kisutch) and Shiner Perch (Cymatogaster aggre-
gata) to Chlorine in Heated Sea-Water." Water Research
14:347-354.
Sugam, R. and G.R. Helz. October 1977. The Chemistry of Chlorine
in Estuarine Waters. Prepared for Maryland Power Plant Siting
Program by Chemistry Dept., University of Maryland.
Thatcher, T., J. Bridge and D. Wood. 1976. "Relative Sensitivity
of Pacific Ocean Coastal Organisms to Power Plant Biocides
and Metalic Effluents, and the Combined Effects of these
Chemicals and Temperature Alteration." IN: Pacific Northwest
Laboratory Annual Report for 1975 to the USERDA Div. of
Biomedical and Environmental Research, BNWL-2000, PT-2,
Battelle Pacific Northwest Laboratory, Richland, WA.
Thatcher, T.O. 1978. "The Relative Sensitivity of Pacific
Northwest Fishes and Invertebrates to Chlorinated Seawater."
IN: Water Chlorination: Environmental Impact and Health
STfects. R.L. Jolley, H. Gorchev, and D.H. Hamilton (eds.)
Ann Arbor Science. Vol. 1. pp. 341-350.
-196-
-------
United States Department of the Interior. 1967. Pollutional
Effects of Pulp and Paper Mill Wastes in Puget Sound.
Walden, C.C. 1976. "Review Paper: The Toxicity of Pulp and
Paper Mill Effluents and Corresponding Measurements Proced-
ures." Water Research V61. 10:639-664.
Walden, C.C. and D.J. McLeay. 1974. Interrelationships of
Various Bioassay Procedures for Pulp and Paper Mill
Effluents. CPAR Report No. 165-1. Canadian Forestry, Ottawa,
Canada.
Walden, C.C., D.J. McLeay and D.D. Monteith. 1975. "Comparing
Bioassay Procedures for Pulp and Paper Effluents." Pulp
and Paper Mag. Canada 76:T130-T134.
Washington State Department of Ecology. July 1974. Acute Toxicity
Bioassay Test Method.
Williams, R.W., W.E. Eldridge, E.M. Mains, A. Reid. 1953. A
Preliminary Report of an Investigation of the Toxic Effects
of Sulfite Pulp Mill Waste Liquor on Downstream Salmon
Migrants in Brackish Water. Washington State Pollution
Control Commission, Tech. Bull. 1-8. 46 pp.
Wilson, M.A. and C.I. Chappell. 1973. Reduction of Toxicity
of Sulphite Effluents. CPAR Report No. 49-2. Canadian
Forestry Service, Ottawa, Ontario.
Woelke, C.E. 1960. Effects of Sulfite Waste Liquor on the
Normal Development of Pacific Oyster (Crassostrea gigai*)
Larvae. Res. Bull. No. 6. State of Washington Dept. of
Fisheries.
Woelke, C.E. 1965. Bioassays of Pulp Mill Wastes with Oysters,
Biological Problems in Water Pollution, Third Seminar.
Tech. Report No. 999-WP-25. Robert A. Taft Sanitary Engin-
eering center, U.S. Public Health Service, Cincinnati,
Ohio.
Woelke, C.E. 1968. Development and Validation of a Field
Bioassay Method with the Pacific Oyster, Crassostrea gigas,
Embryo. Ph.D. Dissertation, University of Washington,
Seattle, Washington.
Woelke, C.E. 1976. Measurement of Water Quality with the
Pacific Oyster Embryo BioassayI Water Quality Criteria,
ASTM STP 416. Am. Soc. Testing Materials, Philadelphia, PA.
-197-
-------
Woelke, C.E., T.D. Schink, E.W. Sanborn. 1970. Development of
an In-situ Marine Bioassay with Clams. Ann. Rep. to the
U.S. Fed. Water Quality Admin., Dept. of the Interior
Grant No. 18050 00J, Washington, D.C.
Woelke, C.E., T. Schink, and E. Sanborn. 1972. Effect of Bio-
logical Treatment on the Toxicity of Three Types of. Pulping
Wastes to Pacific Oyster Embryo. Report Prepared under
EPA contract No. 68-01-377. Washington , D.C.
-198-
-------
VI. BIOLOGICAL RESOURCES
This section discusses the existing literature and data relating
to marine biological resources in the Bellingham Bay area
(Figure VI-1). Much of the detailed information has been placed
in the Appendices G - R. This section contains only summary
statements and tables. In order to key into the ecological dis-
cussion of Chapter VII, the organisms using the waters of
Bellingham Bay are divided into the following groups:
A. Phytoplankton and other aquatic
plants
B. Zooplankton
C. Shellfish
D. Other Invertebrates (crustaceans,
benthos, etc.)
E. Fish
F. Wildlife
Organisms within these groups form the major functioning portion
of the marine (and tributary stream) ecosystems. An inventory
of major organism types occurring within the Bellingham Bay area
is presented in Table VI-1. The study area, which includes
Bellingham, Samish and several smaller bays is shown in Figure VI-1.
The literature and data pertaining to these organisms are dis-
cussed in some detail in the sub-sections below.
A. PHYTOPLANKTON AND MACROPHYTES
Phytoplankton are microscopic plants suspended in marine and
estuarine water that form an integral part of the aquatic foodwebs.
Macrophytes are macroscopic marine algae found predominantly in
the inter- and subtidal regions of marine and estuarine waters.
They are an important contributor to productivity in the area by
virtue of the habitat, feeding and rearing grounds they provide
for a large number of marine organisms. Below is a discussion of
the occurrence and abundance of these two important groups of
primary producers in Bellingham Bay.
-199-
-------
Table VI-1 MAJOR ORGANIC GROUPS OCCURRING IN BELLINGHAM BAY
Number of
Group Sub-group known genera
Phytoplankton
Diatoms
—
Macro algae
Rhodophyta
>1
Chlorophyta
2
Phaeolphyta
1
Zooplankton
Ichthyoplankton
>1
Microplankton
—
Other zooplankton
69
Shellfish
Subtidal hardshell clams
3
Softshell clams
2
Cockles
1
Invertebrates
Mollusca
82
Annelida
78
Arthropoda
34
Nematoda
3
Echinodermat-a
18
Cnidaria
6
Ctenophora
2
Chordata
5
Fish
Marine
66
Anadromous
9
Marine Mammals
Seals
1
Whales and porpoises
3
Marine Birds
Waterfowl and allied water birds
28
Shorebirds
20
Gulls and allies
14
Raptors
4
Marsh birds
3
Diving birds
14
Miscellaneous
4
-200-
-------
Strait of
Georgia
Lummi Bay i
Gooaabarry/ \
vPt.—v ( I
*
t,Munt
iMflm
inHoiiy
San Juan
Islands
0 100 2Q0
'a*Mn«ham
Pt. Frances
Inatl Boy
Chuckanut BayI
Plaaaant Bay
jLBHza lai h__
wildcat CovaV
t
* \
Sinclair
vlal.
Vandovl
lai.
Samiah Bay
Fish Pt.
SamiatT
lai.
0
FMal«o
Bay
ftltWMKW
Padiila Bay
-f
50 150 300
thousands of f««t
Figure
VI-1
BELLINGHAM - SAMISH BAY
BIOLOGICAL
STUDY AREA
-201-
-------
Two major studies have been conducted on phytoplankton productivity
in the Belllingham Bay area (Tollefson 1962 and USDI 1967).
Tollefson's study, authorized and financed by Georgia-Pacific, was
conducted from March 1959 through July 1961. The purpose was to
determine the effect of temperature, salinity and SWL on the
seasonal abundance and composition of phytoplankton. The phyto-
plankton population found in Bellingham Bay can be compared with
phytoplankton populations found in the remainder of Puget Sound
by the U.S. Department of the Interior (USDI). The USDI (1967)
phytoplankton study was a joint WPCC and FWPCA program investigating
the polliitional effects of wastes discharged by seven pulp and
paper mills in Puget Sound. The study began in April 1962 and was
completed in June 1966. One significant objective was to determine
the relation between SSL levels and phytoplankton productivity.
The results of these two phytoplankton studies are discussed later
in this section.
Macrophyte studies in Bellingham Bay provide only minimal detail
on abundances and locations. Three studies that have provided
brief descriptions of Bellingham Bay's macrophytic community in-
clude Harman and Serwold (1975), Webber (1977), and Smith (1976).
Harman and Serwold (1975) assessed the impact of oil on Northern
Puget Sound habitats due to the possible increase in oil tanker
traffic. During the course of their study they located several
kelp and eelgrass beds along Bellingham Bay's shoreline. Webber
(1977) also gives reference to major eelgrass beds in his
literature survey of water quality and biological habitats of
Bellingham Bay. Smith (1976) studied the benthic communities of
Rosario Straits for Washington State Department of Ecology's
(DOE) oil baseline program and furnished information on the location
of a few alga in the Bay area. These three accounts are by no
means a complete inventory of the macrophytic community present
in Bellingham Bay, but they do serve to form a general overview.
-202-
-------
The major phytoplankton found by Tqllefson (1962) in the Belling-
ham Bay region (Figure Appendix G-l) were predominantly sessile
and pelagic diatoms. Below is a list of the dominant (88% of total)
and less dominant (10% of total) forms found:
Table VI-2
MAJOR AND MINOR PHYTOPLANKTON GENERA OF BELLINGHAM
BAY
Dominant
>ccorieis (S)
rragilaria (S)
Nitzschia (S)
Navicula (S)
Melosira (P)
Thalassiosira (P)
Skelotonema (P)
Less Dominant
Biddulphia (S)
Licmophora (S)
Melosira (S)
Coscinodiscus (P)
Chaetocerus (P)
S = Sessile
P » Pelagic
Source: Tollefson 1962
Tollefson found the sequence of seasonal progression for the most
dominant forms to be the following (Tollefson 1962):
January:
February:
March:
April:
May:
June:
July:
August:
September:
October:
November:
December:
None listed
Nitzschia
Nitzschia, Thalassiorsira
Nitzschia, Thalassiorsira, Skeletonema
Buddulphia, Thalassiorsira, Skeletonema, Melosira,
Coscinodiscus
Buddulphia, Skeletonema, Melosira, Coscinodiscus
Cocconeis, Fragilaria, Licmophora, Melosira, Coscin-
odiscus, Nitzschia, Chaetoceros
Cocconeis, Fragilaria, Licmophora, Nitzschia,
Chaetoceros, Navicula
Cocconeis, Fragilaria, Licmophora, Nitzschia,
Chaetoceros, Navicula
Chaetocerus, Navicula
None listed
None listed
-203-
-------
More detail on phytoplankton seasonality can be found in Appendix G
(Table G-2) .
Temperature and salinity were found to be the two primary factors
affecting phytoplankton productivity in all areas of Bellingham
Bay. Temperature and salinity both have a positive effect on phyto-
plankton production. Temperature was found to exert approximately
four times as much effect on the diatom populations as salinity
(Table G -2). Tollefson found a stimulation effect by SSL on
phytoplankton production, with a maximum resulting increase of a
few percent. This, increase may be due to nutrients such as wood
sugars present in SSL; however, Tollefson does not state this.
Tollefson (1962) does state, however, that increased productivity
is a tentative conclusion and subject to some question. He con-
cludes that the phytoplankton populations, in terms of both total
numbers and generic composition present in Bellingham Bay are
within the natural ranges of the remainder of Puget Sound, and
must accordingly be considered normal.
Tollefson's (1962) conclusions on SSL effects differ considerably
from the results of a phytoplankton investigation performed by
the USOI in 1967. Their study related the phytoplankton produc-
tivity and SSL levels in Bellingham Bay (Figure VI-2). The
phytoplankton productivity rate for each of the 10 stations was
as follows:
Station Rate (mg Chl.a/m3/hr) Station Rate (mg Chl.a/m3/hr)
1 1.4 6 2.0
2 4.8 7 2.5
3 3.1 8 1.8
4 2.4 9 2.6
5 1.3 10 3.5
Productivity was low at stations nearest Georgia-Pacific (1 and 5).
The authors concluded that phytoplankton were continuously swept
throughout the study area by water currents and that once the cells
contact high concentrations of SSL O50 ppm), they are physiologi-
cally injured and fail to function normally. This injury does not
directly alter community structure because new phytoplankton are
-204-
-------
Strait of
Georgia
Lummi Bay ( / Unrni
Portag*
UMnmfc
Eliza isL
Sinclair
1st.
San Juan
Islands
Vandovi
Isl.
Fidalgo
Bay
100 200
Seorgia-PacifiCL
'Batttngham
, 6«- V
Chuckanut Bay \
Plaaaant Bay
k9
8'
Samisti Bay
i (
Samish
Isl.
50 150 300
thousands of feet
Padilla Bay
*
Figure VI-2 PHYT0PLANKT0N AND ZOOPLANKTON SAMPLING STATIONS IN
THE BELLINGHAM AREA.
Source: OSDI 1967
-205-
-------
continually being .swept into the area. The data in Figure VI-3
and Table VI-3 show that phytoplankton do sustain injury at SSL
concentrations greater than 50 ppm. The average SSL concentra-
(
tions in the northeast quarter of Bellingham Bay in 1959 -1961
were greater than 50 ppm (Figure VI-4); consequently, a large area
of Bellingham Bay has historically been inimical to phytoplankton.
Levels above 50 ppm have continued into the 1970's, even after the
installation of primary treatment at Georgia-Pacific in 1973
(see Chapter IV : Water Quality).
The limited data on Bellingham Bay macrophytes include reports by
Smith (1976) of the presence of Ulva sp. in Samish Bay and
Monostroma sp. and a variety of red algae in the Lummi West har-
bors . Kelp beds, found predominantly in deeper waters, have been
located along the southern coastline of Lummi Island (Harman and
Serwold 1975).
One of the more important plant species found in the Bay area is
eelgrass (Zostera sp.). Eelgrass is not a marine algae, but
rather, is a vascular plant that is tolerant of salt water and
submergence. Eelgrass is found for the most part in the saline
portions of estuaries, usually below the lowest tide level.
According to Webber (1977), eelgrass is found only in areas of
high water quality. Webber (1977) reports eelgrass beds along
the southerly portion of Portage Island, Eliza Island, Edgemoor
Lagoon and Post Point (see also Figure VII-1). Harman and Ser-
wold (1975) also found eelgrass in Chuckanut Bay and Samish Bay.
Eelgrass beds are an extremely important contributor to pro-
ductivity of the Puget Sound marine system mainly by virtue of
the habitat, feeding, and rearing grounds it provides for a large
number of marine organisms.
In summary, diatoms compose a major fraction of Bellingham Bay's
phytoplankton population. Production was found to be lowest in
the winter and highest in the summer, with temperature and
salinity being the two primary factors affecting their productivity
(Tollefson 1962). Tollefson concluded that the phytoplankton
-206-
-------
2.50
>»
£
a
o
w
o
0»
E
2.00 « -
¦o
m
X
o
a
tm
9
O
a
E
1.50 • -
o
3
"O
O
1.00
0.50
¦ ¦ •
•• •
• •
/>
* ••
• •
o
e
• •
I I I l I I I I I I H—I
50
100
150
200 250 300
SSL Concentration |ppm|
Figure VI-3
THE RELATIONSHIP OF PHYTOPLANKTON PRODUCTIVITY RATE.
PER MG OF CHLOROPHYLL A VS. SSL CONCENTRATION FOR
SAMPLES COLLECTED AT THE SURFACE AT TEMPERATURES
EQUAL TO OR GREATER THAN 10° IN THE BELLINGHAM STUDY
AREA. Source: USDI 1967
-207-
-------
Table VI-3 SUMMARY OF PHYTOPLANKTON PRODUCTIVITY RATE PER UNIT
OF CHLOROPHYLL A (mg carbon fixed/m3/hr/mg Chi.a)
ASSOCIATED WITH THE THREE BROAD RANGES OF SSL ~
CONCENTRATION OBSERVED IN THE BELLINGHAM AREA.
Samples taken at the surface at temperatures equal
to or greater than 10 C.
SSL concentration Range
Statistic
0-50 ppm
51 - 100 ppm
Greater than
100 ppm
Range
0.25 to 2.28
0.25 to 1.15
0.08 to 0.71
Mean
0.90
0.64
0.44
Median
0.80
0.56
0.51
Sources USDI 1967
-208-
-------
Strait of
Georgia
Lummi Bay , / tonum
ftan
y*«on
/
Sattfogham
Portage Bay y\Portage
Isl
Chuckanut'say
Wildcat Cove
Sinclair
Isl
San Juan
Islands
Vendovi
Isl.
Samish Bay
Samish
Isl.
Fidalgo
Bay
Anacortaa
Padilla Bay
100 200
50 150 300
thousands of feet
Figure VI-4 AVERAGE SURFACE SSL IN THE BELLINGHAM STUDY AREA —
DATA FROM UNIVERSITY OF WASHINGTON STUDY OF NOVEMBER
1959 - NOVEMBER 1961.
Source: USDI 1967
-209-
-------
population in Bellingham Bay was within the natural ranges found
in the remainder of Puget Sound. Tollefson (1962) and the USDI
(1967) differ in their findings of SSL effects on phytoplankton
production. Tollefson feels that production is stimulated by
SSL, whereas the USDI concludes that phytoplankton sustain injury
upon contact with SSL. with respect to Bellingham's macrophytic
community, the species composition has not been adequately in-
vestigated. A partial inventory, however, does document the
presence of numerous eelgrass beds along the coastal area and a
few red, green and brown algae.
B. ZOOPLANKTON
Zdoplankton (minute animals which float or drift passively in
the water) feed mainly on phytoplankton and are therefore a very
important link between primary producers and the commercially
valuable fish in the Strait and the Puget Sound basin. Zooplankf
ton can be divided into three main categories:
• Ichthyoplankton
• Microplankton
• Other Zooplankton
Ichthyoplankton include the eggs and larval forms of the fish
and shellfish, many of which are commercially important. Micro-
plankton refers primarily to protozoan (one-celled) and metazoan
(many-eelled) organisms which are found in marine waters. Other
zooplankton refers to all other minute animals inhabiting the
marine waters. The vertical and horizontal distributions of
zooplankton in the marine waters are dependent upon several
factors, including season, location, illumination, time and
hydrographic conditions, and numerous physical factors.
1. , Ichthyoplankton
Ichthyoplankton occurring in the Bellingham area are predominantly
those of flounder species (mostly right-eyed flounders) common
to Puget Sound. Commercially, the most important is the English
sole (Ward, Robison and Palmen 1964). The USDI (1967) conducted
-210-
-------
a study on English sole eggs to determine the distribution and
abundance of the eggs in the Bellingham area. The study was con-
ducted from January through March 1966. Plankton samples were
collected at ten stations in northern Bellingham Bay (Figure VI-5)
at depths of 1, 17 and 33 feet. The English sole eggs fraction
was removed and measured by volume. Simultaneous water samples
were taken with Nansen bottles from the three depths just prior
to each tow and analyzed for salinity and SSL. It was found
that significant numbers of English sole eggs were present in the
surface waters of Bellingham Bay during the peak of the reproduc-
tive season (Table VI-4). It is important to note that these
large numbers of eggs occur in waters with high SSL concentration.
This finding prompted further study on the relationship between
SSL and English sole egg development. The bioassay results
of this study have been discussed in detail in Chapter V.
2. Microplankton
Microplankton in the Bellingham Bay region include:
Sessile forms (stationary) Pelagic forms (mobile)
Stalked sessile ciliates Tintinnids
Foraminifera Ciliates
Silicoflagellates Silicoflagellates
The sessile forms are low in number in the late winter or early
spring (range from 0 to 50 per square mm), increasing in July
through December (about 10 to 150 per square mm) (Tollefson 1962).
The numbers of pelagic plankton are comparatively constant through-
out the year (1000 to 5000 per liter) with the exception of a
late summer peak in August (approximately 20,000 per liter) (Tollef-
son 1962). Tintinnids are dominant during the first half of the
year with ciliates and silicoflagellates peaking in the late
summer.
Two factors, temperature and SSL, have been shown to affect
microplankton productivity in Bellingham Bay (Tollefson 1962).
-211-
-------
0 1000 2000
4000
500 1500 3000 yards
Bellingham
Lununt
Indian
faservatiorv
Portage
Luanroi M.
Bellingham
Bay *7
10
Point
Frances
.8
Chuckanut
Bay
PlMUM
Governors Bay
Point
Figure VI-5 STATION LOCATIONS IN THE BELLINGHAM AREA AT WHICH
FLATFISH EGGS WERE COLLECTED AND WATER QUALITY WAS
DETERMINED.
Source; USDI 1967
-212
-------
Table VI-4 FLATFISH EGG DISTRIBUTipN IN THE BELLINGHAM AREA,
Inarch 2, 1966
Station
Depth
Temp.
Salinity
Specific
SSL
Volume of
(ft.)
(°C)
(°/oo)
Gravity
(ppm).
eggs (ml)*
1
1
6.6
25.5
1.0200
55
0.9
17
7.1
26.8
1.0210
19
0.5
33
7.1
27.0
1.0211
12
1.0
2
1
6.6
23.7
1.0186
179
1.8
17
6.8
27.0
1.0212
51
1.8
33
7.1
27.0
1.0211
9
0.5
3
1
5.5
24.2
1.0191
175
0.5
17
6.6
26.9
1.0211
106
0.5
33
6.6
27.0
1.0212
20
5.5
4
1
6.2
25.2
1.0198
83
5.8
17
6.6
26.7
1.0210
28
1.0
33
7.0
27.3
1.0214
13
0.7
5
1
6.4
25.4
1.0200
94
1.7
17
6.7
27.2
1.0214
25
0.6
33
7.0
27.4
1.0215
11
0.6
6
1
4.5
19.8
1.0157
61
1.3
17
6.3
26.0
1.0205
35
1,6
33
6.5
26.4
2.0207
8
0.9
7
1
5.6
24.4
2.0193
60
3.5
17
6.5
26.8
1.0211
41
2.1
33
6.8
27.6
1.0217
18
0.5
8
1
6.1
25.0
1.0197
83
3.5
17
6.8
27.0
1.0212
34
0.8
33
6.9
27.1
1.0213
17
0.8
9
1
5.0
21.3
1.0169
73
0.5
17
6.7
26.3
1.0206
60
4.3
33
6.7
28.9
1.0227
16
0.7
10
1
4.9
22.5
1.0178
69
0.3
17
6.5
26.5
1.0208
64
10.0
33
6.7
27.3
1.0214
10
1.5
*.
One ml contains approximately 1000-1200 fertilized English sole eggs
Source: USDI 1967
-213-
-------
Tollefson found temperature to be the dominant regulator demon-
strating a positive correlation with microplankton productivity.
He also concluded that field concentrations of SSL have a stimu-
j
lating effect on protozoan growth in Bellingham Bay with a
significant regression of +0.0015 protozoa (log values) per ppm
SSL. Within the dispersion area in the head of Bellingham Bay,
this represents an increase of 18% in the protozoa population.
For all other areas the increase would be about 2%. Tollefson
states that the increases are referred to as "associated" in the
opinion that they are secondary results following bacterial
increases (food supply) created by the organic enrichment.
Two foraminif&ral studies have been conducted in the Bellingham
Bay area: one in 1959 (Sternberg 1967) and another in 1973
(Scott 1973). Sternberg's objective was to acquire an understanding
of sediment distribution in Bellingham Bay. He collected 82
sediment samples and determined the percent foraminifera for
various areas within the Bay region. Concentrations of foramini-
feral tests varied from 0-6% by weight in the sediments, the
highest being in the center of Bellingham Bay, and 2 - 4% by
weight in the mouth of Samish Bay. No foraminiferal species
were identified.
The objective of Scott's (1973) study was to compare the fora-
miniferal fauna present in Puget Sound deep waters with those
found on the Samish and Padilla tidal flats. Scott found that
Miliammina fusca is abundant in both locations while Trochammina
pacifica is dominant only in the deep waters. Scott did not,
however, offer suggestions as to why this variation in species
composition occurred.
3. Other Zooplankton
The sessile forms found in Bellingham Bay by Tollefson (1961)
include (see also Table H -1):
hydroids
nematodes
barnacles
worms
bivalves
crustacea
-214-
-------
Hydroids and nematodes account for 58% and 29% of the total
sessile forms, respectively.
The dominant pelagic forms are:
Annelids Copepods
Cladophora Copepod nauplii
Barnacle nauplii TUnicates
Flatworms
Copepods, Copepod nauplii and tunicates are the most abundant,
accounting for 84% of the total dominant forms.
The seasonal progression of zooplankton species listed above are
as follows (Tollefson 1962) (see also Table H-l);
January:
None listed
February:
None listed
March:
None listed
April:
Barnacles, Tunicates, Copepods
May:
Tunicates, Copepods
June:
Zooplankton in general, Tunicates, Annelids, Copepods
July:
Hydroids, Tunicates, Annelids, Copepods
August:
Tunicates, Annelids, copepods
September:
Annelids, Copepods
October:
Copepods
November:
None listed
December:
None listed
A more recent study by the USDI (1967) sampled zooplankton at
10 stations within the Bellingham - Samish area (Figure VI-2).
Samples were collected at the surface and at 20 feet. A list
of the species found during this investigation is presented in
Table VI-5. Zooplankton concentration (organisms/m3) is
considerably greater at 20 feet than at the surface of the water
(Table VI-6). Webber (1975) found the same to be true, statin-
that rich distributions of zooplankton are present beneath the
freshwater and SSL layers.
-215-
-------
Table VI-5 FAUNAL LIST OF THE BELLINGHAM ZOOPLANKTON
Copepoda
Aeartia clauai
Aeartia danae
Aeartia longiremus
Aeartia tonaa
Aetideua armatua
Aetideopsis roatrata
Calanus criatatua
Calanua finmarchieua
Calanua plumchrus
Candacia columbiae
Centropagea memurrichi
Clau30calanu8 areuieornia
Corycaeua affinia
Epilabidocera amphitritea
Euoalanua bungii
Others
Appendicularia (Tunicata)
Chaetognatha (arrow worm)
Ctenophora
Doliolida (tunicata)
Euphausiacea
Evadne sp. (cladocera)
Gammaridae (Amphipoda)
Hyperiidae (Amphipoda)
Isopoda
comb jellies
flatworms
Eurytemora sp.
Harpacticoida
Metridia luaena
Microcalanua pu8illua
Oithona aimilia
Oithona apinivo8tria
Oncaea sp.
Paracalanu8 parvua
Pareuchaeta japonica
Paeudocalanua minutus
Scolecithricella minor
Tortanua disoaudatu8
Copepodites
Nauplius larvae
Mysidacea
Natantia (shrimp)
Noatiluca sp. (Dinoflagellata)
Ostracode
Podon sp. (Cladocera)
Salpa sp. (tunicata)
Siphonophora (jelly £ish)
Medusae (jelly fish)
Nematodes
Pre-adult forms (other than Copepoda)
Anomura megalops (crab)
Anomura zoea (crab)
Amphipoda larvae
Brachyura megalops (crab)
Brachyura zoea (crab)
Callianaaaa sp. larvae (ghost
shrimp)
Cirripedia cypris (barnacle)
Cirripedia nauplius (barnacle)
Cyphonautes larvae
Euphausiacea calytopsis
Euphausiacea furcilla
Fish egg
Fish larva
Gastropoda larva
Mitraria larva
Mysidacea larva
Pelecypoda larva
Pluteus larvae
Polychaeta larvae
Natantia larva (shrimp)
Upogebia sp. larvae (ghost shrimp)
Copepod nauplii
Sources USDI 1967, Tollefson 1962
-216-
-------
Table VI-6a MEAN VALUES OF PROPERTIES MEASURED AT THE SURFACE IN THE BELLINGHAM AREA;
PLANKTON STUDY OF AUGUST 1964 - JULY 1965. Source: USDI 1967
Stations
Property
1 2
3
4
5
6
7
8
9
10
Salinity (°/a>)
25.7 26.9
24.6
28.1
26.5
28.2
28.8
28.0
28.8
29.1
SWL (ppm, 10% Solid Sol.)
334 54
38
14
85
17
5
7
8
6
Zooplankton Concentration
(organisms/m3)
6518 2345
2474
2113
4203
4079
6436
5673
2579
1436
Table VI- 6b MEAN VALUES
OF PROPERTIES
MEASURED
AT 20
FEET IN
THE BELLINGHAM
AREA:
PLANKTON STUDY OF AUGUST 1964 - JULY 1965
Source: USDI
1967
Stations
1 0
•>
C
£
*7
8
10
Property
X z
Salinity (°/no)
28.9 29.0
27.9
28.9
29.0
29.1
29.2
29.1
29.1
29.4
SWL (ppm, 10% Solid Sol.)
22 11
18
8
13
6
4
5
6
5
Zooplankton Concentration
5221 5054
8515
3401
6131
6338
9723
4796
5815
5218
(organisms/m3)
Refer to Figure VI-2
-------
The USDI (1967) monitored both salinity and SSL for each sample
station (Table IV-6) but there does not appear to be any strong
correlation between these parameters and zooplankton abundance.
Salinity ranges from 24.6 - 29.4 °/oo for both surface and 20
foot samples. Freshwater stress, therefore, does not appear to
be a limiting factor. SSL levels, however, are greatest at the
surface and may account for the lower zooplankton concentrations.
On a station to station basis, SSL levels are not inversely
related to zooplankton concentration. Instead, the station with
the highest zoopi^;, ,,* concentration has the highest SSL concen-
tration.
C. SHELLFISH
This discussion will center on those shellfish that are of com-
mercial value, namely the edible mollusks. Shellfish feed by
filtering particulates from the surrounding water. This method
of feeding enables them to concentrate trace substances present
in the water, including toxic contaminants. Bioaccumulation
of such contaminants may pose a potential threat to human con-
sumers and, therefore, must be closely monitored.
Shellfish found in the Bellingham area include:
Subtidal hardshell clams
Butter clams (Saxidomus cfiqanteus)
Manila clams (Venerupis japonica)
Littleneck clams (Protothaca staminea)
Horse clams (Tresus sp.)
Softshell clams
Eastern softshell (Mya arenaria sp.)
Bent nose (Macoma nasuta)
Cockle (Clinocardium nuttallil
The principal subtidal hardshell clam beds (butter and little-
neck clams) are located in Hale Passage, Sinclair Island and
Guemes Island (Figure VI-6) (Goodwin and Shaul 1978a and b) .
Table VI-7 lists the acreage of each bed, the number of pounds of
butter and littleneck clams present and the total clam density
-213
-------
Nook«mcx R-lvw
Strait of
Georgia
Lummi Bay
l I Lamnu
Indian
vMion
Bettmgtram
m
Portaga
Chuckanut Bay
Plaasant Bay
ItMM
Eliza IsL
Wildcat Cov*
Sinclair
Isl
San Juan
Islands
Vandovi
Isl.
Samislt Bay
Samish
Isl.
Fidalgo
Bay
Padilla Bay
100 200
50 150 300
thousands of feet
Figure VI-6 SHELLFISH BEDS NEAR HALE PASSAGE, SINCLAIR ISLAND AND
GUEMES ISLAND
Source: Goodwin and Shaul 1978
-219-
-------
Table VI-7 SHELLFISH BEDS IN THE BELLINGHAM BAY REGION
Source: Goodwin and Shaul 1978
(See Appendix J for reference to designated figures and sample numbers)
lbs lbs Density
Location Acreage Butter Littleneck lbs/ft*
Hale Passage 150 2,487,886 1,505,826 0.6
(Figure J-l)
(Sample #*s 13-19)
Hale Passage 166 1,514,843 649,218 0.3
(Figure J-l)
(Sample #'s 31,
33-38)
Sinclair Island 280 7,305,012 852,251 0.7
(Figure J-2)
(Sample #'s 6-9)
Guemes Island 847 10,698,380 386,910 0.3
(Figure j-2)
(Sample #'s 1-5,
7-10, 16, 19)
-220-
-------
in metric (english) units. More detail on the numbers and
densities of clams for Hale Passage, Bellingham Bay, Sinclair
Island and Guemes Island can be found in Appendix J (Table
J-l and Figures J-1 and J -2) .
Webber (1977) reports low densities of butter clams and horse
clams, in the Nooksack delta. Macoma and Mya are found east and
west of the Nooksack delta, but once again their abundance is
very low. Post Point harbors littleneck clams, cockles, butter
clams, horse clams, Mya and Macoma clams; however, the area is
located close to a sewage treatment plant and therefore is posted
as polluted. Recreational digging is most common in the
northern portion of Chuckanut Bay east of the rail right-of-way.
Littleneck clams, butter clams, cockles and the two softshell
clams are found there.
D. OTHER INVERTEBRATES
Invertebrates are a diverse group of organisms. They are predom-
inantly bottom dwellers, highly specialized to adapt to the rocky,
sandy and muddy substrate typical of the temperate zone shore-
lines. They vary in size from a few millimeters to several
decimeters and inhabit an area extending from high tidemark to
deep waters. The benthic fauna is an integral part of the food
web and has commercial and recreational importance.
Invertebrates found in and around Bellingham Bay include eight
phylums:
• Mollusca - shellfish
• Annelida - segmented worms
• Arthropoda - lobster, crab, shrimp, isopods
• Nematoda - roundworms
• Echinodermata - starfish, sea urchins
• Cnidaria - anemones
• Ctenophora - jellyfish
• Chordata - tunicates
composed of 230 species as outlined in Appendix H (Table H -1).
-221-
-------
Invertebrate studies performed in the Bellingham Bay region
include:
A report by the USDI (1967) investigating water
pollution in Puget Sound.
A report prepared by Nelson (Nelson et al. 1974) on
mercury in the benthos of Bellingham Bay.
A record of the number of crab caught in the Bell-
ingham - Samish area from 1943-1975 (Evans and
Moos 1976).
A study by CH^M Hill (1974) in which abundance and
diversity of benthos off Post Point were monitored
from September 1973 to August 1975.
A study of the effect of SSL on the distribution of
the ectoprocta (Schizoporella unicornis) in Bellingham
Bay, providing a short list of species (Ross & McCain 1976).
A literature search prepared by Webber (1977) which
briefly describes the benthos of Bellingham Bay and
provides a short list of species.
An environmental impact statement prepared by the
City of Bellingham (1978) for Georgia-Pacific's
proposed.biotreatment lagoon, outfall and diffuser;
to treat and discharge process effluent from their
Bellingham sulfite pulp, paper and chemical complex.
Subtidal and intertidal benthic studies in con-
junction with periodic dredging of three navigation
waterways in the Bay (Webber 1978).
For convenience in the evaluation of biological communities in
the Bay area, the area of Bellingham Bay in the vicinity of the
City of Bellingham will be considered a separate entity, "Inner
Bellingham Bay", is defined as that area easterly of a line be-
tween Post Point (Latitude 48° 43' 10" N; Longitude 122° 30'
50" W) to the cement plant (Latitude 48° 46' 6" N; Longitude
122° 31' 20" W) (Webber 1977) (Figure VI-7).
1. Organism Diversity
In general, Bellingham Bay has a rich variety of benthic inver-
tebrates due to the generally good water quality and substrate
conditions in ,the outer Bay area. The inner Bay, including inner
1.
2.
3.
4.
5.
6.
7.
8.
-222-
-------
0 1000 2000
4000
500 1500 3000 yards
Jfootoack R]y«r
Belllngham
irrrn
Lummi
Indian
Reservation
Bellingnam
Bay
Portage
Frances
Chuckanut
Lummi **!•
Governors
Point
Figure VI-7 DIVERSITY INDICES OF INVERTEBRATES IN THE BELLINGHAM
BAY REGION
Sources: Nelson et al. 1974, CH2M Hill 1974
Webber 1977. 1978
-223-
-------
and central Whatcom -Waterway, I & J Waterway and inner Squalicum
Waterway, however, is heavily affected by industrial pollutants
and has a lower diversity and abundance of organisms (Figures Vi-7
and VI—8) (Webber 1977, 1978). Low abundance and diversity in
the Bellingham Bay region are not solely the result of industrial
activity. Reduction in surface salinity by freshwater drainage
in some portions of the Bay stress many intertidal organisms. A
list of invertebrate species documented in the Bellingham Bay
region appear in Table H -1, Appendix H . Abundance values for
all invertebrates listed are not available. Catch data for crabs
in the Bellingham - Samish area from 1943 - 1975 appear in Table Vl-8.
More specifically, an increase in organisms diversity with increasing
distance from the industrial shoreline of Bellinghami Bay has been
demonstrated by Nelson (Nelson et al. 1974) using the Shannon
diversity index:
H = - i (n^/N) In (n^/N)
where n„* = the number of individuals in the ith species, and
N = total number of individuals,
A species diversity index expresses the relationship between the
number of species present and the total number of organisms. Any
strong, limiting factor, whether biological, physical or chemical,
can reduce or eliminate sensitive species. This results in
fewer species, which gives a lower diversity index for the same
number of organisms. Five stations monitored in the Whatcom
Waterway had diversity indices of 0.0 (Figure VI-7). Two samples
taken in the area of the proposed lagoon for Georgia-Pacific
(Figure VI-8) had indices of 0.0 and 0.28. Extending seaward
from the inner Whatcom Waterway area, conditions improved,
reaching a diversity of 2.3 in the outmost reach of the waterway.
Along the route of the proposed Georgia-Pacific outfall (Figure
VI-7), Nelson (1974) reports diversity increasing from 0.3 near
the seaward side of the proposed lagoon to values of 2.0 near
the end of the outfall diffuser. Webber (1978) reports that
intertidal species richness was lower than subtidal species rich-
-224-
-------
Squaficum
Martoa
B«liingham
•13
16
• Bellingham
Bay
Gaorgia- Pacific , f
42
26
0 200 400 750 yards
100 300 500
1000
Figure VI-8 AVERAGE TOTAL NUMBER OF INVERTEBRATE SPECIES FOUND IN A
TRIPLICATE SAMPLE TAKEN IN 1977.
Source: Webber 1978.
-225-
-------
Table VJ-8 CRAB LANDINGS IN BELLINGHAM - SAMISH AREA IN
NUMBER OF CRABS
Year
Number
Year
Number
1943
49,058
1959
127,228
1944
148,233
1960
219,097
1945
264,667
1961
262,122
1946
367,871
1962
204,679
1947
275,492
1963
414,695
1948
301,901
1964
365,595
1949
166,669
1965
320,511
1950
216,712
1966
215,204
1951
211,799
1967
275,584
1952
164,077
1968
245,659
1953
137,328
1969
258,163
1954
85,900
1970
180,425
1955
39,254
1971
227,479
1956
27,683
1972
270,899
1957
33,796
1973
170,969
1958
85,355
1974
84,893
1975
150,960
Source: Evans & Moos 1976
-226-
-------
ness in Bellingham Bay. In an undisturbed environment, species
diversity in an intertidal region is usually greater than that
of a subtidal region. Low intertidal diversity reported by
Webber (1978) may be due to greater exposure of intertidal organ-
isms to surface water, which contain the highest concentration
of total mill effluents (as measured by the PBI test).
Further studies on diversity off Post Point have been conducted
by CH2M Hill (1974) for Georgia-Pacific. Post Point is the site
of the Post Point Pollution Control Plant which treats sewage and
industrial waste from the City of Bellingham before it is dis-
charged into the inner harbor. Diversity (Figure VI-9) and
abundance of benthic organisms were monitored in the area from
September 1973 to May 1975. Average values for both seasonal
and spatial variation in diversity appear in Table VI-9. Figure
vi-10 portrays an apparent seasonal pattern. Diversity peaks
in late winter and spring and decreases in summer and autumn.
The diversity appears to be slightly lower in the northern
sample locations off Post Point, which may be indicative of an
effluent and freshwater gradient extending from the industrial
inner harbor (Figure VI-9 ). Spatial and seasonal variation in
abundance was also monitored (Table VI-10). Once again a seasonal
pattern appears (Figure VI-11). Abundance peaked in fall and
winter and decreased to a minimum in late winte-r and spring.
Spatially, abundance was lowest close to the Post Point shoreline
and increased with distance from the point.
Abundance studies by the City of Bellingham (1978) have shown
that organisms are noticeably scarce on the impervious berm
which makes up most of the intertidal zone adjacent to the pro-
posed Georgia-Pacific lagoon. Pilings in the lagoon area and
waterway are generally free of marine growth, although recent
damage to pilings by marine borers suggest possible improvement
in water quality. The distribution of Schizoporella unicornis,
an encrusting lower intertidal to shallow subtidal cheilostome,
•also reflects the impact of industrial effluents (Ross and McCain
-227-
-------
4000
0 1000 2000
S00 1500
3000 yards
Noofcseck
Bellingham
Lumnri
Indian
Reservation
Belllngham
Bay
POST
Portage
Point
Frances
Chuckanut
Bay
Luonmi frt,
Pleasant
Governors £\ say
Point
Figure VI-9 SAMPLE STATION LOCATIONS FOR THE CH2M HILL STUDY
ON ABUNDANCE AND DIVERSITY OF BENTHOS OFF POST
POINT
Source: CH2M Hill 1974
-228-
-------
Table VI-9. CH2M HILL DATA FOR EIGHT LOCATIONS OFF POST POINT
(Refer to Figure VI-10)
S - 1
Diversity Index (d) =
log N
e
Date
Stations
Average
Diversity
/Month
12 Oct
73
2.01
2.23
-
-
2.40
2.16
0.76
2.23
1.97
29 Jan
73
1.67
1.57
0.42
3.34
1.84
1.81
1.21
2.01
1.96
28 Mar
73
1.55
1.08
2.22
2.83
2.13
2.04
1.37
2.00
1.90
10 Sep
73
1.6
1.35
0.18
0.92
1.18
1.82
0.71
-
1.11
01 Nov
73
2.18
2.22
1.32
2.39
2.06
1.48
1.46
-
1.87
14 Feb
74
2.59
1.48
2.83
2.91
1.28
1.11
2.01
-
2.03
24 Apr
74
2.93
3.34
1.29
3.82
1.34
1.26
2.38
-
2.34
25 Jun
74
0.87
2.16
1.56
1.44
2.39
0.91
0.0
-
1.33
29 Aug
74
2.08
-
1.44
-
1.77
0.75
-
1.76
1.56
29 Oct
74
1.72
1.92
1.31
2.86
1.82
1.42
1.63
0.91
1.70
21 Feb
75
2.73
2.79
1.50
2.89
2.34
2.89
1.54
1.01
2.21
06 May
75
1.81
2.53
1.64
3.69
2.18
2.16
1.70
2.55
2.28
AVERAGE DIVERSITY
PER SITE
1.98
2.06
1.52
2.59
1.89
1.65
1.34
1.78
Source: Hill 1974
-------
Oft 2.50'
0.00
1972 1973 1974 1975
Month
Figure VI-10 DIVERSITY INDEX PERIODICITY OF BENTHIC
INVERTEBRATES OFF POST POINT FROM 1972 - 1975
Source: CH2M Hill 1974
-230-
-------
Table VI-10.
CH2M
HILL DATA
FOR
EIGHT LOCATIONS
OFF
POST POINT:
NUMBER
OF
ORGANISMS
PER
SITE
(Refer
to
Figure VI-
U)
Date
Stations
1
2
3
4
5
6
7
8
Monthly
Average No.
of Organisms
13 Sep
72
-
-
17
35
-
-
-
26.0
12 Oct
72
12
6
-
!-
8
4
14
6
8.3
29 Jan
73
6
24
11
20
15
48
27
15
20.8
28 Mar
73
26
16
15
25
42
19
39
19
25.1
10 Sep
73
12
9
248
232
70
9
17
-
85.3
01 Nov
73
25
58
44
43
30
57
31
-
41.14
14 Feb
74
22
15
24
22
23
90
7
-
29.0
24 Apr
74
41
16
47
39
42
24
19
-
32.6
25 Jun
74
10
4
13
69
11
3
1
-
15.9
29 Aug
74
18
38
64
15
52
55
-
30
38.9
29 Oct
74
603
8
21
47
3
69
40
3
99.3
21 Feb
75
3
6
28
16
13
8
7
53
16.8
06 May
75
48
35
39
15
62
65
19
34
39.6
AVERAGE NUMBER OF
ORGANISMS/SITE
23.8 19.6 47.6 48.2 30.9 37.6 20.1 22.9
Source: C^M Hill 1974
-231-
-------
100
90
80
70
60
50
40
30
20 ¦
10'
0<
s'o'n'd'j'f'm'a'm1 j'j'a's'o'n'dIj'f'm'a'm'j'j'a's'o'n'dIj'f'm'a'm'
1972 1973 1974 1975
Month
'igure VI-11 ORGANISM ABUNDANCE PERIODICITY OFF POST
POINT FROM 1972 - 1975
Source: CH2M Hill 1974
-232-
-------
1976) . Schizoporella unicornis occurs at stations on or near
Bellinghaxn Bay where tjie spent sulfite liquor in the surface
water layer averages 40 to 50 ppm (data from USDI 1967). It
does not occur where spent sulfite liquor is 100 to 200 ppm
(Figure VI-4).
Nelson (1974) divided Bellingham Bay into four areas based on
similarity of benthos habitation. The equation for similarity
is:
Similarity = Z(2W)
KA+B)
where W = the sum of the smaller of shared species scores
A = the number of species in sample A
B = the number of species in sample B
The results are illustrated in Figure VI-12. Group A, the
Whatcom Waterway area, has a low diversity (0.0 - 0.45) and
is dominated by the hardy annelid Capitella capitata. Group
B, adjacent to Whatcom Waterway, is dominated by the annelids
Capitella and Terebellides and the molluscs Macoma and Mitrella.
Diversity is high, 1.4 - 2.3. This high diversity is unexpected,
for it occurs in an area stessed by freshwater and industrial
activity. Group C, northwest of Whatcom Waterway, is domin-
ated by the annelids Owenia and Maldanidae and the echinoderm
Amphiota. The mollusc Yoldia and the clam Pinnexa also appear
here. The moderately low diversity of 0.45 - 1.4 may be a re-
sult of industrial stress. Group D, north of Post Point,
contains the annelids Maldaidae and Glycinde. The molluscs
Axinopsida and Yoldia and the echinoderm Amphiota are also pres-
ent. The cobble beach areas in this region receive limited
salinity stress and are moderately rich, intertidal communities.
The diversity ranges from 1.2 - 2.3. The rocky beaches of
Chuckanut Bay, Lumni Island and Eliza Island have the greatest
diversity of infauna (Webber 1977)CFigure VI-1). Gravel, sand & muddy
beaches of Chuckanut Bay are the best shellfish habitats. The
northerly beaches and beaches of Lummi Peninsula and Portage
Island all receive high freshwater influence and have low
diversity and density of intertidal organisms (Webber 1977).
-233-
-------
1000 2000
4000
500 1500 3000 yards
ttoofcfticK Wwr
Lurnint
Indian
Reservation
Portage
Bay
% \ Portagelst
Lummi ftk
Point
Frances
Belilitgliant
Bellingham
Bay
Key
A Low diversity, annolids.
B High diversity, annelids
and molluscs.
C Low diversity, annollda,
molluses and scWnodoriws.
D Hlflh diversity, annelids,
molluscs and schlnodorms.
Chuekanut
Bay
Governors
Point
Figure VI-12 AREAS OF SIMILAR FAUNA AND DIVERSITY IN BELLINGHAM
BAY
Source: Nelson et al. 1974
-234-
-------
Beach transect profiles describing the major intertidal habitat
types in Bellingham Bay appear in Figures K-l through K-6 in
Appendix K (Webber 1977). These profiles help define which ben-
thic species associate with particular substrate types.
2. Sludge beds
In Whatcom Waterway (Figure VI-13) the discharge of volatile
suspended solids by Georgia-Pacific resulted in a sludge deposit —
an oxygen deficient layer of decomposing organic material. This
sludge buildup had to be dredged periodically by Georgia-Pacific
to maintain adequate water depth in their log pond. Prior to
February 1969, the dredge spoils were disposed of off Post Point
(Figure VI-14) (Poston, letter of July 31, 1968).
Deposits of sludge often have a deleterious effect on the natural.
benthic community. Sludge deposits physically alter the sub-
stratum, eliminating many of the indigenous organisms through
burial and suffocation, in some cases, decomposition of the
organic material causes depletion of dissolved oxygen along with
increases in hydrogen sulfide and ammonia. These conditions often
eliminate all traces of benthic life.
A study performed by the USDI (1967) in 1964 and 1967 clearly
showed that the sludge deposit in Whatcom Waterway had an adverse
effect on the benthic community in that area. Very few benthic
organisms were found in the inner Whatcom Waterway where sludge thick
ness was greatest and the sediment volatile solids were 30% (Fig-
ures VI-13, VI-15). As sludge thickness and volatile solids de-
creased, an increasing number of benthos was found, but these were of
one kind (worms). Outside the areas of heavy sludge accumulation,
the size and diversity of the benthic community sharply increased.
Georgia-Pacific's present NPDES permit prohibits the disposal of
solid waste in state waters. It is assumed> although not verified
by correspondence that Georgia-Pacific is complying with present
solid waiste disposal guidelines and no longer has a sludge bed
buildup problem.
-235-
-------
Etelfingfcam
Vertical Transect graphed below
0* 3
Pacific
Legend
0 200 400 750 yarda
100 300 500 1000
a. inches of Sludge
End B
at Sample Station
Vertical Transact of Sludge Bad Thickness
3000 2000 1000
Dlatance a tang Whatcom Waterway In feet
End B
End A
Belfinghann
0 200 400 750 yarda
100 300 500 1000
Figure VI-13 SLUDGE DEPOSITS IN WHATCOM WATERWAY AND BELLINGHAM
HARBOR: (A) Sludge Thickness, (B) Percent Volatile
Solids Content of Sludge
Source: USDI 1967
-236-
-------
Bellingham Bay
vl
Sludge Bed
POINT
Bellingham Bay
OINT
B.
O 1000 2000
4000
500 1500 3000 yards
Figure VI-14
CHARACTERISTICS OF BOTTOM SEDIMENTS IN BELLINGHAM HARBOR AND CONTIGUOUS
PARTS OF BELLINGHAM BAY: (A) Percent of Wood Fraction (chips and
fragments) in the sediments, and (B) Percent of Volatile Solids in
the Sediments.
Source: USDI 1967.
-237-
-------
Q.
E
W 140'
u>
£
«
E
«o
c
•
0)
w
O
120'
^ 100- -
E
3
£ 80
60
40
20
•l
4—1—4 1—I
10 20 30 40
PtrcMt Volatile Solids hi
the Sediments 8/11/64
10-
•
' a
o
¦c 9<4—
.
a 8'
E .
«
I 7-
• 6-
»
to
O
0
w 5
A
E
9
1 4
«
5
•_ •
i i i i
10 20 30 40
Percent Volatile Solids in
the Sediments 5/10/66
Figure VI-15 TOTAL NUMBER OP BENTHOS PER SAMPLE VS. PERCENT VOLATILE
SOLIDS IN THE SEDIMENTS OP BELLINGHAM HARBOR
Source: USDI 1967
-238-
-------
E. FISH
The Bellingham study area encompasses the receiving waters of
five Bays. From northwest to southwest these include Portage,
Bellingham, Chuckanut, Pleasant and Sairiish Bays (Figure VI-1) .
The tributaries of all bays except the Samish are considered to
flow directly to Bellingham Bay. Samish Bay is acknowledged as
a separate estuary (coastal body within which seawater is
measurably diluted with fresh water).
There are nine tributaries contributing flow to Bellingham
and Samish Bays. These drainages support nine species of
anadromous fish which require a freshwater environment during
some stages of their life cycle. During their juvenile migration,
anadromous fish utilize the shorelines in the estuarine waters
of the study area for food and protection. In addition to
anadromous fish, 66 marine fish species are known to occur in
Bellingham and Samish Bays.
Both anadromous and marine fish are important in estuarine
ecology. During their respective marine and fresh water life-
cycles, roe (fish eggs) and juvenile fish provide an important
food source for larger organisms in the food chain. Adult fish
consume lower organisms in the food chain and in turn provide
prey to larger fish, mammals and birds.
Three major types of commercial fisheries occur in the study
area. These include trawling, salmon netting, and herring
sac-roe fisheries. Chinook, coho, chum and pink contribute
to the major salmon catch in the area. Significant bottom fish
species in trawl net landings include: English sole, Rock sole,
Starry flounder, Butter sole, Sand sole, True cod, Lingcod,
and a variety of rockfish.
The following information is sectioned into two major parts.
Section 1 provides a brief discussion on fishery studies and
-239-
-------
corresponding methodologies conducted in the Bellingham - Samish
Bay region (1963 - 1978). The subsequent section (2} summarizes
the results of individual studies to provide an inventory of
anadromous and marine fish utilization and distribution in the
study area.
1. Research Methods
Fishery related studies in Bellingham and Samish Bays have been
conducted by federal (FWPCA, FAO), state (WPCC, WDF), regional
(PSTF, PNRBC) and private (FRI, Huxley College, Nooksack and
Lummi tribes) agencies (Table VI-11)(see abbreviations, page ii).
Below, arranged in chronological order, are presented brief
analyses of sampling locations, equipment, and methodology for
each study.
As a result of the joint federal-state Enforcement Conference
(Olympia, Washington, January 16-17, 1962), the Washington State
Enforcement Project (represented by WPCC and FWPCA) initiated
a four year study (1962-1966) to investigate water pollution in
four areas of Puget Sound (USDI 1967). In cooperation with this
project, data on occurrences and migration of juvenile salmon
in Bellingham Bay was collected {April - June 1964).
A beam trawl (9X9 foot) was towed for five minute intervals in near-
surface waters along each of 3 transects (Figure L -1, Appendix L ).
A total of 57 trawl tows were made during May 1964. During
April-June 1964, mobile fish traps were also -towed along 22
transects within Bellingham Harbors (Figure L -2). The fish
trap opening was 12 feet by 1.5 feet. Upon completion of each
of the 10 minute tows (beam trawl and mobile fish traps) the
species of captured fish were counted.
The Fisheries Research Institute (FRI) (April 10 - June 27, 1963)
studied the seaward migration, entry time, schooling and avoid-
ance locations and length of residence of three salmon species
-240-
-------
Table VI-11 FISHERY STUDIES CONDUCTED IN BELLINGHAM AND SAMISH BAYS
Agency
Study Date
Methodology
Reference
WPCC and FWPCA
FRI
April - June 1964
April 10-June 27, 1963
Beam Trawls
Mobile Fish Trap Tows
Beach Seines
Townet
USDI 1967
Tyler 1964
FRI
April 27-June 20, 1967
Townet
Sjolseth et
al. 1970—
PNRBC
WDF
Huxley College
1964 - March 1970
July 1, 1969 - Nov. 1975
April 1974 - March 1975
Analysis of existing data
Field investigation
Analysis of existing data
Field investigation
Beach seine
Trawl net
PSTF and
PNWRBC 1970
Williams et
al. 1975—
Webber 1975
Huxley College
May 1977 - April 1978
Trawl net
Webber 1978
WDF, FAO, and
Nooksack and Lummi Tribes
1972 - 1979
Field observation
Pentilla 1979
-------
(chum, coho, and chinook) in Bellingham Bay (Tyler 1964). Beach
seines and' tow net samples were obtained from nearshore and
offshore locations respectively (Appendix Figure L -3). In order
to determine the time of downstream migration, fyke nets were
placed in tributary streams of Bellingham and Chuckanut Bays
"(Figure L -3) .
During the spring survey, a beach seine net (61 meters long and
3.7 meters deep) was used to conduct 142 seine hauls at 37 lo-
cations. Tow netting was performed from April 16 - May 29, 1963.
The first two surveys (April 16-17 and April 25, 1963) utilized
a small net (2.74 square meters) to establish standard tow
locations. The remaining townet samples were caught with a net
opening measuring 3 meters by 6 meters and a net length of 13.1
meters. The nets were towed at velocities of 0.9 meters/second
for 30 minutes. Fyke nets were stationed in the Nooksack river,
Squalicum, Whatcom, Padden and Chuckanut. Creeks. The nets werei
1.2 square meters at the entrance and 3 meters long.
Sampled fish, both salmon and incidental species (marine and
anadromous trout), were counted, identified and released. Per-
iodically the salmon catch was retained for length measurements
to determine species, age and time of downstream migration.
FRI conducted a water quality study (April 27 - June 20, 1967)
of estuarine nursery areas for juvenile salmon in Bellingham Bay
(Sjolseth et al. 1970). The Bay was divided into 25 townet
sampling sections (Figure L -4). In order to study salmon migra^
tions, a percentage (13.3% chinook, 16.3% coho) of the total
juvenile chinook and coho stock in the Nooksack Hatchery were
marked with fluorescent pigment and released. During the study,
307 tows were conducted within Bellingham Bay. The nets (14
meters long) were towed for 10 minutes, covering a distance of
1170 meters.
-242-
-------
In 1964 the Pacific Northwest River Basins Commission (PNRBC)
initiated a water resource study of the Puget Sound area (PSTF
and PNRBC 1970). One segment of the study and its resulting
report (Appendix XI) describes basin summaries (11 basins) of
fish and wildlife use, their locations and provides a plan for
managing these resources. The study consists of an analysis of
available data on file, supplemented with a 4-year field
investigation of streams in the Puget Sound area. Appendix XI
(PSTF and PNRBC 1970) only provides basin summaries; therefore,
the Washington Department of Fisheries organized a catalog on
10,000 individual streams in the Puget Sound area. The Stream
Utilization Catalog; Vol I (Williams 1975) describes the physical
characteristics and salmon utilization of major streams in a
basin area.
A 1974 - 1975 study (Webber 1975) trawled nine sites every
month (April - March) for demersal (bottom) fish samples (Figure
L -5). Each net had a 10 foot opening and was towed for 10
minutes per station. Beach seines were conducted at six locations
with a 150 foot long, 6 foot deep seine. All sampled fish were
counted, identified, measured and released. Some individuals
were sub-sampled for further analysis.
A subsequent demersal fish study (Webber 1978) on fish occurrence
and abundance in Bellingham Harbor (Figure L -6) was conducted
every 2 to 3 months from May 1977 to April 1978. Trawl samples
were conducted at 5 sites on a regular basis. Three additional
locations were sampled occasionally. The otter trawl net (10
foot opening) was towed for 5 minutes per site. Studies of the
fish catch are analogous to the previous study (Webber 1975).
The WDF, FAO and biologists from the Nooksack and Lummi tribes
have conducted herring spawn surveys in Hale Passage and Samish
Bay since 1972 (Penttila, letter of November 20, 1979). To
produce a medium intensity of spawn along one mile of shoreline
in Washington requires the spawning of 600 tons of herring (Meyer &
Adair 1978). Based on this estimate, the WDF and FAO devised
-243-
-------
standard spawning intensities for eggs per lineal inch and
estimated adult spawning biomass (EASB) (Table VI-12). Utilizing
these standards, an evaluation of spawn intensity provides an
estimate of stock strength (Meyer and Adair 1978).
2. Fish Distributions and Research Results
a. Anadromous Fish Species
.The Bellingham - Samish Bay stuay area is the direct receiving
water for 9 tributaries (Figure VI-16). one river and four creeks
contribute flow directly to Bellingham Bay. From north to south
these include the Nooksack River, Squalicum, Whatcom, Padden, and
Chuckanut Creeks. Samish Bay receives flows from Oyster Creek,
Colony Creek, Edison Slough and the Samish River. The streambed
and flow characteristics of these tributaries is further describe^
in Appendix M .
Each of these rivers or creeks is utilized by one or more of
eight anadromous species. These include:
Coho - Silver Salmon (Oncorhyncus kisutch)
Chum - Dog Salmon (0. keta)
Chinook - King Salmon (0. tshawytscha)
Pink - Humpback Salmon (0. gorbuscha)
Red - Sockeye Salmon (0. nerka)
Steelhead Trout (Salmo gairdneri)
Searun Cutthroat Trout (Salmo clarkii)
Searun Dolly Varden Trout (Salvelinus malma)
Longfin Smelt (Spirinchus thaleichthys)
The fresh water lifecycle for eight of these species is defined
according to location (Table VI-13 and VI-14). In order to spawn
or reproduce, the mature adult anadromous species migrates up-
stream in the original fresh water tributary from which* it
developed. Upon completion of the migration, the adult fish,
utilizes gravel areas to deposit and fertilize eggs. Intra-
-244-
-------
Table VI- 12 STANDARD HERRING SPAWNING INTENSITIES
Intensity Eggs/Lineal Inch EASB*(Tons/Mile)
Very Light (VL)
1 - 20
42.6
Very Light - Light (VLL)
21 - 50
128.4
Light (L)
51 - 90
214.2
Light - Medium (LM)
91 -150
407.4
Medium (M)
151 -230
600.0
Medium - Heavy (MH)
231 -340
942.6
Heavy (H)
341 -500
1285,8
Very Heavy (VH)
> 500
1714.2
* Estimated Adult Spawning Biomass
Source: Meyer and Adair 1978
-245-
-------
gravel development of the young embryo is terminated when the
newly hatched fish (alevin) develops into a free swimming fry
(juvenile fish, usually .25 to .50 mm in length) (USDI 1967,
Scott and Crossman 1975). Depending on the species, the fry
will remain in the fresh water system for one to four years,
or migrate immediately (one to three months) to an estuarine
environment (bays).
Inventory and distribution of anadromoua fish in major
tributaries of Bellingham and Samish Bays
Chinook Salmon: The Nooksack and Samish Rivers are the only
two tributaries supporting major runs by this species (Figure vi-16)
(Williams et al. 1975) .. Spring and Summer-fall Chinook occur
in the Nooksack system; however, summer-fall chinook migrate up
the Samish River. Chinook spawn in the lower 7 (South Fork) to
23 miles (North and Middle Forks) of the Nooksack River and in
the mainstem from the North and Middle fork confluence downstream
to within one mile of Bellingham Bay (PSTF and PNRBC 1970).
Chinook spawn in the Samish River from river mile (RM) 5.0 to
RM 12 (Williams et al.. 1975) .
Adult spring Chinook begin entering the Nooksack River in late
March and continue this migration until early August (Table
VI—.13) when spawning is initiated. Juveniles emerge from
the gravel and remain in the Nooksack system for more than a
year, beginning their downstream migration to estuarine waters
the second spring following hatching.
Summer-fall chinook adults begin their migration up the Nooksack
in July and begin spawning in mid-September (Table VI-13).
Hatching is complete by mid-February and the juveniles begin
their migration to Bellingham Bay within 3 months following
emergence. The major downstream migration occurs during high
water flow (mid-April — early July). The fresh water life cycle
for fall chinook in the Samish River is similar to that occurring
in the Nooksack system (Figure Vi-16).
-246-
-------
c
Figure VI-16
INVENTORY OF SALMON
UTILIZATION IN BELLINGHAM
AND SAMISH BAYS
KEY: Anadromous Species
K . C Chum S Sockoy* L Loogllo Smalt § Anadromous Rih Hatchacy
S Cohy>| P Pink T Staaliwad. Cutthroat, end Dolly Vudrn
D
-------
/ / M /// /////i/f/t/i/Jj/ffj/f/j,
Summer-Fall
Chinook
3-5
Years
Upalraam Migration
Spawning
MntinM Omtopdwal
Juvanlla Raarlng
—
MM
——1
—
—
—
—
Coho
3-4
Years
Upalraam Migration
Spawning
Inlragraval Davalopmanl
Juvanlla Hatting
Juvanlla Oul Migration
MB
=
MM
MM
MM
mm
mm
mmmm
mm
Chum
3-5
Years
Uptliaam Migration
Spawning
Inlragraval Davalopmanl
Juvanlla Raarlng
Juvanlla Oul Migration
_
a
ss
¦Sm
^¦11
——
Sockaya
3-6
Years
. Uptlraam Mlgialloa
Spawning
Inlragraval Oavatopmanl
Juvanlla Raarlng
=
—
mmm
MM
¦
—
—
Spring
Chinook
3-5
Years
Uptlraam Migration
Spawning
Inlragraval Davalopmanl
Juvanlla Raarlng
—
—
—
—
"=
=
SLh
m^m
Pink
2
Years
Juvanlla Out Migration
Uptliaam Migration
Spawning
Inlragraval Davalopmanl
Juvanlla Raarlng
_
mm
—
—
¦
ss
Sm
MM
MM
Summer
Steelhead
4-6
Years
Uptliaam Migration
Spawning
Inlragraval Davalopmanl
-
—-
SS5
—
as
—
—
-
Winter
Steelhead
4-6
Years
Juvanlla Oul Migration
Upilraam Migration
Spawning
Inlragraval Oavtlopmanl
Juvanlla Raarlng $
Juvanlla Out Migration
_
¦
...
_
ammm
¦"
—
HlilHlllI
sz
zzz
ss
sa
SLdi
Searun
Cutthroat
3-4
Years
Uptliaam Migration
Spawning
Inlragraval Davalopmanl.
Juvanlla Raarlng $
Juvanlla Oul Migration
=
=
n
=
=
=
Zmmm
—
mm
P
Table VI-13 FRESH-HATER LIFE CYCLE OF SALMON AND ANADR0MOUS ~TROUT SPECIES IN FRESH-HATER TRIBUTARIES
FLOWING TO BELLINGHAM BAY
Source: Puget Sound Task Force and the Pacific Northwest River Basins Commission 1970,
Williams etal. 1975.
Normally extends over a two year period.
-------
Summer-Fall
Chinook
Upaliaam Mlgtalkm
Spawning
Inliagiaval Oavalopoianl
Juvanlla Riving
Juvanlla Out Ulg(llhN)
Coho
3-4
Years
Upaliaam Migiallon
Spawning
Inliagiaval D«alopoianl
Juvanlla Raailng
Juvanlla Out Migiallon
Chum
3*5
Years
Upsliaam Migration
Spawning
Inliagianl Pavalopmanl
Juoanlla Raailng
Juvanlla Oul Migration
I
to
¦t*
V£>
I
Searun
Cutthroat
3-4
Years
Upil'aam Migiallon
Spawning
Inliagiaval Oavatopoianl
Juvanlla Rawing %
Juvanlla Oul Migration
Searun
Oolly
Varden
5-6
Years
Upaliaam Mlgrattoa
Spawning
Intiagraval Davatopmanl
Juvanlla Rawing ^
Juvanlla Oul Migiallon
Summer
Steelhead
4-6
Years
Upaliaam Migiallon
Spawning
Inlragi aval Oavalopmanl
Juvanlla Rawing ~
Juvanlla Oul IMgfalhm
Winter
Steelhead
4-6
Years
Upaliaam Mtgralioa
Spawning
Intiagiaval Davalopoianl
Juvanlla Raailng $
Juvanlla Oul Migiallon
Table VI-14 FRESH-WATER LIFE CYCLE OF SALMON AND ANADROMOUS TROUT SPECIES IN FRESH-
WATER TRIBUTARIES FLOWING TO SAMISH BAY
Source: Puget Sound Task Force and the Pacific Northwest River Basins
Commission 1970, Williams 1975
~Normally extends over a two-year period.
-------
Every year the Washington State Department of Fisheries (WDF)
estimates the natural escapement (number of returning wild stock
fish) of various salmon species for selected tributaries. From
1965-1976, the yearly escapement average for summer-fall Chinook
was 2,944 and 1,033 fish for the Nooksack and Samish Rivers
respectively (Appendix N, Table N-l) (Geist 1979, Phinney 1977).
The- WDF maintains two salmon hatcheries in the study area. The
Nooksack Salmon Hatchery is located on Kendall Creek, a tributary
flowing into the North Fork of the Nooksack River (Figure VI-16).
This facility handles two salmon species, fall chinook and coho.
The Samish River's hatchery is located on Friday Creek (RM 1.5)
(Figure VI-16). This tributary flows into the Samish River
at RM 10.5. Fall chinook, chum and coho salmon are spawned in
this hatchery. The total artificial escapement (1965-1976) (returning
hatchery stock) for fall chinook averaged 1,216 fish/year and
3,395 fish/year for the Nooksack and Samish Hatcheries,
respectively (Table N-2) {Rasch and Foster 1978). The Lummi
Indian Tribe maintains a salmon hatchery (Lummi Hatchery) on
Skookum Creek. Coho, chum and chinook salmon are spawned in the
hatchery; however, artificial escapement numbers for this
facility are unavailable.
Coho salmon: Coho salmon utilize all 9 tributaries in the study
area (Williams et al. 1975). Both the Nookaack and Samish Rivers
support the largest migrations. Spawning grounds on the Nook-
sack are concentrated in areas of channel splitting. This occurs
all along the North Fork, the lower South and Middle Forks,
and along the upper portions of the mainstem of the Nooksack
River. Approximately 22 miles of the mainstem of the Samish
River (total length 29.1 miles) are accessible to coho salmon.
Concentrated coho spawning areas are located between RM 5.0
and RM 12.0 (Williams et al. 1975).
Coho begin entering the Bellingham Bay tributaries in mid-July
(Table VI-13). By the middle of November the migrating salmon
commence spawning which continues into January. At the
-250-
-------
completion of intragravel development the fry remain in fresh
water for & year and migrate downstream during the annual spring
runoff.. Compared to the Bellingham system, Samish Bay drainages
maintain shorter adult coho migration periods. (mid-August - October)
(Table VI-14'J . Spawning and intraqravel development begins in
mid-October and fry emergence is relatively complete by mid-April.
From 1965-1978 natural escapement for the Bellingham and Samish
Bay drainages averaged 5,298 coho/year (Table N -1) (Zillgis
1979), Artificial escapement from 1965-1976 averaged 3,460
coho/year for the Nooksack Hatchery. The Samish Hatchery
averaged a return of 16,911 coho/year for the same period
(Table N -2) (Rasch and Foster 1978).
Chum salmon: The lower segments of Bellingham and'Samish Bay drainages
are utilized by chum salmon (Williams et ad. 1975) . In the Nookse^
River, spawning occurs in riffles and side channels of the Nortk,
Middle and South Forks and the mainstem within 1 mile of
Bellingham Bay (PSTF and PNRBC 1970). Squalicum, Whatcom and
Padden Creeks provide spawning grounds in intermittent stream
sections. Chum salmon spawning in Chuckanut Creek is concentra-
ted in the lower .5 miles of the tributary (Williams et al. 1975).
Lower portions of Oyster and Colony Creeks are utilized by these
fish with a high coho concentration in the lower tributaries of
Colony Creek. The Samish River supports spawning chum through-
out most of its mainstem and its lower tributaries (Williams et al.
1975) .
Adult chum begin entering the Bellingham Bay drainages in mid-
September (Table VI-13) . Spawning is initiated by mid-November
and continues into January. Fry begin to emerge in March and
by mid-May their downstream migration is complete. The Samish
Bay tributaries have a shorter upstream migration period which
continues through November (Table VI-14). Fry development and
downstream migration begins in March and is complete by early
May.
-251-
-------
During 1968 to 1978 the average natural chtun escapement (TableN-1)
(Ames 1979} for the study area averaged 29,100 chum/year.
The Samish Hatchery (1965-1976) averaged a return of 620 chum/
year (Table N-2} (Rasch and Foster 1978).
Pink salmon: The Nooksack River is the only tributary in the
area supporting a permanent run of pink salmon (Williams et al. 1975) .
Occasional pinks have been recorded in the Samish River and
other tributaries of Bellingham and Samish Bays but no established
migrations are known to exist. Spawning areas are concentrated
in the upper reach of the North Fork, lower reaches of the Middle,
and South Forks and the channel splitting areas in the Nooksack
mainstem (Williams et al. 1975).
Adult pink salmon only enter the Nooksack River in odd-numbered
years. Migration begins in mid-July and continues until mid-
August (Table VI-13). Spawning commences in late August and fry
begin to emerge in late February. At this time, the young fish
begin migrating to an estuarine environment. By mid-May
downstream migration is relatively complete.
A natural stock average of 50,350 fish/year (from 1959-1977)
returns to the Nooksack River during migrating years (Table N-l)
(Ames 1979). Fink salmon are not spawned in either of the two
salmon hatcheries in the study area; therefore, there is no
artificial enhancement of pinks.
Sockeye salmon; The North Fork of the Nooksack River is the only
tributary in the area known to support a run of Sockeye salmon.
The small migration spawns approximately 60 miles upstream from
Bellingham Bay in a .5 mile side channel (Williams et al. 1975).
Sockeye begin their migration in the Nooksack by mid-July (Table
VI-13). Spawning commences in early September and terminates
by mid—October. Fry emergence is complete by February and these
fish remain in. the fresh water system for more than a year.
Migration to an estuarine environment begins the second spring
after emergence.
-252-
-------
Steelhead. trout: The Nooksack and Samish Rivers support large
winter and summer steelhead runs; however, small migrations
(20-100 fish) also utilize the remaining independent drainages
of Bellingham and Samish Bays (WDG 1962-1977, PSTF and PNRBC
1970). The winter steelhead provides the most productive run
size of the two species (Table N-3) (WDG 1962-1977). The
spawning fish are located in the tributaries and mainstem
reaches while rearing areas occur in shallow sheltered sections
of the drainages. Rearing occasionally occurs in ponds and
.lakes in the stream system (PSTF and PNRBC 1970).
Summer steelhead enter the Nooksack and Samish Rivers in mid-
April (Tables VI-13 and VI-14). This migration is complete
October. Spawning occurs early the following spring (late
February) (Withler 1966). Intragravel development is complete
by mid-August. The fry remain in this system 1-4 years before
migrating to the Bay areas in March and April.
Winter steelhead migrate from November to May (Tables VI-13 and
VI-14). Spawning begins in mid-December and the fry emergence is
complete by mid-June (Samish River) and mid-August (Nooksack River).
The juvenile fish remain in the freshwater for 1-4 years followed
by an early spring downstream migration.
Steelhead punch cards retrieved from anglers by the WDG (1962-
1977) provide an estimated steelhead catch return for the Nooksack,
Squalicum, Chuckanut and Samish drainages (Table N-3). During
this 15 year period, catch data indicates a general decline in
winter steelhead migrations in the Nooksack and Samish Rivers
(Table N-3) .
There is an increase in the 1977-1978 winter run catch for the
Samish River but future data is required to determine if the size
is increasing.
The Bellingham Fish Hatchery located on Whatcom Creek is managed
by the WDG for the rearing of steelhead trout. The Hatchery does
not have any returning runs but maintains a brood of stock (fish
-253-
-------
retained for spawning) to produce fry. The juvenile fish are then
planted in selected areas.
Searun cutthroat trout; These fish are present in all accessible
drainages in the study area; however, the Nooksack River supports
the largest run (PSTF and £>NRBC 1970, Johnson 1979). In the
Bellingham Bay tributaries, searun cutthroat migrate from mid-
June until mid-April the following year (Table VI-13V. Spawning
begins in December and fry development is complete by early August.
In the Samish system upstream migrations begin much later
(October) and extend into January (Table VI-14). Spawning
season is shorter (December — mid-May) and fry emerge by May.
The fry remain in freshwater 1-3 years. At this time, the fish
migrate to an estuarine environment.
A fishtrap recently located on the Samish River is maintained
by WDG. This is the only means of estimating searun cutthroat
returns to the study area. In 1978, 600 adult cutthroat re-
turned to the Samish River (Johnson 1979).
Searun Dolly Varden Trout: Anadromous Dolly Varden Trout are
known to occur in the large tributaries that have deep pools
adjacent to shallow gravel areas (PSTF and PNRBC 1970). Fresh-
water life cycles of the Dolly Varden are only available for the
Samish River (Table VI-14). There are no established totals on
adult returns on file at the WDG.
Long fin Smelt; The only other anadromous species to occur in
the study area is the longfin smelt (Spirinchus thaleichthys).
The Nooksack River supports an anadromous run of this species.
Upstream migration begins in early October and continues until
early December. These fish usually spawn in the lower 3 miles
of the Nooksack, remaining within the rsinge of tidal influence
(Pentilla, letter of November 1979). There have been no
extensive studied conducted by regulatory agencies to indicate
the fresh and marine water life cycles of this species.
-254-
-------
a. Migration Patterns of, Anadromous Fish
Downstream migration of juvenile anadromous species occurs during
high river flow (March - July) (PSTF and PNRBC 1970). Upon enter-
ing an estuarine system (Bellingham and Samish Bays), both fry
and smolts (downstream migrating anadromous salmon and trout,
1-3 years of age) locate along the shoreline (Scott and Crossman
1975) . Pink, chum and fall Chinook enter the Bay as small fry
and usually remain nearshore for a longer period of time than
species migrating as smolts (coho, sockeye, spring Chinook and
steelhead) (USDI 1967). During their salt water life stage#
coastal cutthroat and Dolly Varden remain along or within a short
distance of a river's mouth (Scott and Crossman 1975).
Salmon migration studies of fry and smolt in Bellingham Bay were
performed sporadically from 1964 to 1970 (Tyler 1964, USDI 1967,
and Sjolseth et al. 1970). Beach seines, townets (Tyler 1964,
Sjolseth et al. 1970), beam trawls and mobile fish traps (USDI
1967) were used to determine the migration area of juvenile sal-
mon in the Bay.
Juvenile salmon migrate (April - June) along the western, northern
and eastern shorelines (0.5 miles or less from coast) of Bellingham
Bay (Figure VI-17) (Sjolseth et al. 1970). This is verified by
increased townet catches along the shorelines compared to a
decreased abundance in the Bay (Figures N-l, N-2, Tables N-4, N-5).
The northern shorelines, of Bellingham Bay include the inner Bay
or Harbor area. During their seaward migration, juveniles from
the Nooksack River and Squalicum Creek pass through this area but
are found to avoid the inner Whatcom Waterway (Figures N-l and
N-2) (USDI 1967).
Juvenile chum salmon concentrate within Portage Bay, along eastern
Portage Island, eastern Bellingham Bay from northeast Post
Point to Chuckanut Bay, Eliza Island, and InatiBay (Figure VI-17)
(Tables n-4 and N-6)' (Tyler 1964) . Emergent size chums (34-38
mm) sampled along the east side of Portage island are believed
to originate from the Nooksack River (Tyler 1964).
-255
-------
Legend
1000 2000
4000
¦ a Chums
500 1500 3000 yards
Chinnook
Beiiingham
Lummi
Indian
Ras«rvation
Baliingnam
Bay
Point
Frances
Chuckanut
URTtnH t*t
Governorsfr^v
Point
NoU-Actufll Location
ot eiua id.
Figure VI-17 CHUM, CHINOOK AND COHO CONCENTRATED MIGRATION
AREAS IN BELLINGHAM BAY
Source: Tyler 1964, Sjolseth et a.1. 1970
-256-
-------
Chum salmon caught nearshore (beach seine) were usually smaller
(65 mm or less) than those sampled offshore (townet). Tyler
concluded that smaller migrating fish remain nearshore until
obtaining a larger size at which time they migrate to deeper
water.
Areas dominated by migrating juvenile chinook include the east
side of Portage Peninsula northward along the shoreline to
Squalicum Creek and the northeast area of Bellingham Harbor to
Post Point (Figure VI-17, Tables N-4, N-5, n-6) (Tyler 1964,
Sjolseth et al. 1970).
Cohd catches indicate relatively equal distributions along the
shallow coasts of Bellingham Bay. A slightly elevated catch,
number occurred along the east side of Lummi Peninsula and the
northeast area of inner Bellingham Bay (Figure VI-17, Tables
N-4, N-5, N-6) (Sjolseth et al. 1970).
d. Marine Fish
During the 1963 (Tyler 1964) migration survey (April - June 1963)
of juvenile salmon in Bellingham Bay, 30 marine and 3 anadromous
trout species occurred as incidental fish in the sampling nets
(Table VI-15). According to findings of updated surveys (Webber
1975, Webber 1978) 47 additional demersal and nearshore marine
species are represented in the Bay (Table VI-15).
Demersal fish collected by otter trawls in Bellingham Bay
indicate a relatively uniform distribution of individual species
composition and abundance among sampling stations throughout
the area (Webber 1975). Results of the 1977-1978 fish survey
in Bellingham Harbor (inner Bellingham Bay) indicate a high
species richness in outer Whatcom Waterway (13 species) (Table
N -7, Figure L-6) (Webber 1978). The inner Whatcom Waterway
had no species occur during sampling (Webber 1978).
-257-
-------
Table VI-15 MARINE SPECIES OCCURRING IN BELLIN.GHAM BAY
Common Name Scientific Name Reference
Northern Anchovy Engraulia mordax 1
Cabezon . Soovpaeniahthya ma,vmovatue 2
High cockscomb Anoplarohua purpuraaeens 2
Pacific dogfish Squalis .suakleyi 1
Spiny dogfish Squalis aoanthias 2, 3
Blackberry eelpout Lycodopaia paoifiaua 2, 3
Shortfin eelpout Lyaodea brevipea 2
Wattled eelpout Lyaodea palearia 2
Arrowtooth flounder Atkereates atomiaa 2
Starry flounder Platiah.th.ya stellatu3 1, 2, 3
Bay goby Lepidogobiua lepidus 2, 3
Crescent gunnel Pholia laeta 2
Kelp greenling Hexagrammoa deaagvammus 1
White-spotted Eexagrammoa atelleri 1, 2
greenling
Penpoint gunnel Apodiahthya flavidua 1, 2
Saddleback gunnel Pholia avnata 2
Pacific hake Merluaaium produatus 3
Pacific herring Clupea harengua pallaaaii 1, 2, 3
Red Irish lord Bemilepidotua hemilepidotua 1
Pacific lamprey Entoaphenua tridentatua 1
Sand lance Ammodytea hexapterus 2
Lingcod Ophiodon elongatua 1
Spiny lumpsucker Eumicrotremua orbia 2
Plainfin midshipman Poriehthya notatua 2, 3
Pile perch Rhaooohilua vacoa 2
Shiner perch Cymatogaater aggregata 1, 2, 3
Striped perch Embiotoaa lateralie 1, 2
Bay pipefish Syngnathua griaeolinatua 1, 2
Speamose poacher Agonopaia emmelane 2
Sturgeon poacher Agonua acipenaerinua 2, 3
Tubenose poacher Pallaaina bafbata 2
Snake prickleback Lumpenu8 aagitta 1/ 2
White-barred prickle- Porodinus rothroeki 2, 3
back
Ratfish Bydrolagua colliei If 2
Black rockfish Sebaatodea melanopa 1
Copper rockfish Sebaatodea caurinua 1
Rosethorn rockfish Sebaatea helvomaoulatua 2
Yelloweye rockfish Sebaatea ru.bberrimu8 2
* Chinook salmon Qnahorhynchua taahawytaaha 2
Pacific sanddab Cithaviahthy a atigrmeua 2
Speckled sanddab Cithaviehthya aovdidua 2
Pacific sandlance Ammodytss hsxapterus 1
Buffalo sculpin Enophvya biaon 1, 2, 3
Great sculpin Myozocephalua polyaehtho- 2
dephalua
Manacled sculpin Synohirua gilli 2
Padded sculpin Avtediua feneatralia 2
continued
-258-
-------
Table VI-15 Continued
Common Name Scientific Name Reference
Roughback sculpin Chitonotus pugeteraia 2
Roughspine sculpin Tviglops maaellus 2
Sailfin sculpin Nautiohthya oculofaaoiatus 2
Sharpnose sculpin C-linooottua acutioeps 2
Silverspotted sculpin Bl.epsi.aa oirrhosus 2
Slim sculpin Radulinua asprellua 2
Smoothhead sculpin Artediua lateralia 2
Soft sculpin Gilbevtidia aigalutes 2
Spinyhead sculpin Paaycottus aetiger 2
Staghorn s6ulpin Leptoeottua armatua 1, 2, 3
Tadpole sculpin P3ychrolute8 paradoxus 1, 2
Tidepool sculpin Oligooottua maculo8ua 1, 2
Pile seaperch Pamaliahthya Vacca 1
Daubed shanny Lumpenus maoulatua 2, 3
Longfin smelt Spirinohus thaleichthy8 2, 3
Surf smelt Hypomeaus pretiosus 1, 2
Tidepool snailfish 0ligooottu8 maoulo8us 1, 2
Butter sole laopaetta isolepia 2
C-0 sole Pleuronichthy8 aoenoaus 2
Dover sole Micro8tamu8 paoifious 2
English sole Pavophrys vetulus 1, 2, 3
Flathead sole Rippoglo8aoide8 elaasodort 2
Rex sole Glyptoeephalu8 zachirus 2
Rock sole Lepidop8etta bilineata 1, 2, 3
Sand sole Paettiohthys melanoatiou.8 2, 3
Slender sole Lyopsetta exilia 2
Three-spined stickle- Ga8tero8teus aauleatua 1, 2
back
Pacific tomcod Miorogadus proximus 1, 2, 3
Cutthroat trout Salmo olavki 1, 2
Steelhead trout Salmo gairdneri 1/2
Tubesnout Aulorhynahua flavidu8 1, 2, 3
Dolly Varden Salvelinua malmo 1
* The text does not total these
anadramous fish with marine
species.
Reference Key:
1 Tyler 1964
2 Webber 1975
3 Webber 1978
-259-
-------
Nearshore fish sampled by beach seines represent both demersal
.and neritic (shallow waters over continential shelf) fish. As
in demersal fish, individual nearshore species composition is
uniform throughout sample sites in the Bay; however, abundance
does vary (Webber 1975). Webber (1975) indicates that nearshore
fish are more abundant at specific southern locations (Stations
1 and 6) of the Bay than'in northern areas (Table N-8, Figure
L -5). Threespine stickleback are dominant along the shorelines
of Portage Island, Post Point, Chuckanut Bay and Eliza Islands
(Tyler 1964 and Webber 1975).
Seven dominant species were found to compose 1% or more of trawl
and beach seine samples (April 1974 - March 1975) in Bellingham
Bay (Table VI-16).(Webber 1975). Commercial fisherman trawl
landings (1975-1977) of food fish in the Bay indicate eight
additional dominant marine species occur in the area (Table vi-16)>.
Six marine species dominanted survey trawl catches (May 1977 -
April 1978) within Bellingham Harbor (Table VI-16) (Webber 1978).
Studies on individual marine species have been confined to
baitfish (Pacific herring, northern anchovy, and Pacific sand-
lance) ; however, the Pacific herring has received primary inves-
tigation. The WDF, U.S. Fish and Wildlife Service (Fisheries
Assistance Office (FAO)) and biologists from the Nooksack and
Luirani tribes have been conducting herring spawn surveys since
1972 (Penttila,letter of November 1979).
Research results in the Bellingham - Samish area indicate her-
ring spawning ground areas exist in the littoral zone (between
high and low tides) of Hale Passage, Portage Bay and northern
Samish Bay. A summary of the 1972-1978 Hale Passage spawning
ground surveys and their locations are provided in Table VI-17
and Figure Vl-18 respectively. Spawning ground data in Samish
Bay is incomplete. A single survey was conducted each year by the WDF
(.1973-1977) (Penttila, letter of Nov. 20, 1979). Each of these surveys
revealed a spawn intensity of "trace" to "very light" (1-50 eggs/sq.
inch or 42.8 spawner tons/mile)(Pentti la, letter of November 1979).
-260
-------
Table VI-16 DOMINANT MARINE FISH IN BELLINGHAM BAY
Common Name Scientific Name Reference
Tr\ie cod
Gadua maorocephalus
1
Ling cod
Ophiodon elongatus
1
Starry flounder
Platiahthys stellatus .
1, 2,
Pacific herring
Clupea havengua palldaii
3
Shiner perch
Cymatogaater aggregata
2
Sturgeon poacher
Agonus aaipenaevinua
2
Snake prickleback
Lumpenus sagitta
2
Staghorn sculpin
Leptoaottus armatus
2, 3
Butter sole
Iaopaetta iaolepia
1
English sole
Parophrya vetulua
1, 2
Rock sole
Lepidopsetta bilineata
1
Sand sole
Paettichthya melanoatieua
1, 3
Longfin smelt
Spirinoh.ua thai ei ah thy a
3
Pacific tomcod
Microgadua proximua
2, 3
Other rockfish
1
Reference Key:
1 Pattie and Gormley 1977, Pattie 1978, Pattie and Gormley 1978
2 Webber 1975
3 Webber 1978
-261-
-------
Table VI-17 SUMMARY OF SPAWNING ACTIVITIES IN HALE PASS
Source: Penttila, letter of November 20, 1979
Documented
Estimated Spawner
Herring Spawning
Herring Biomass
Dates
Tons
May 11, 1972
603
May 5-6, 1972
2690
1972 TOTAL
3293
April 27 - 30, 1973
(a)
3358
May 10 & 18, 1973
(b)
573
1973 TOTAL
3931
February 22-27, 1974
145
May 2-4, 1974
3726
June 3, 1974
155
1974 TOTAL'
4026
March 1-2, 1975
109
April 23, 1975
131
May 13 - 15, 1975
834
May 15 - 19, 1975
1166
1975 TOTAL
2240
April 22-24, 1976
(a)
1100
April 28 - 29, 1976
(a)
650
May 6, 1976
(b)
695
May 18-22, 1976
(b)
584
1976 TOTAL
3029
April 11 - 12, 1977
(a)
30
April 13, 18, 1977
(a)
268
April 19, 1977
(a)
1412
April 23, 1977
(a)
768
May 3-9, 1977
(b)
957
May 11-14, 1977
(b)
345
May 18-24 & June 6,
1977
(b) 150
1977 TOTAL
3930
April 7 - 13, 1978
(a)
852
April 22, 1978
(a)
19
May 1 - 2, 1978
(b)
445
June 8, 1978
(b)
27
1978 TOTAL
1343
April 11, 1979
15
April 14-17, 1979
483
May 2-4, 1979
320
May 24, 1979
40
1979 TOTAL
858
-262-
-------
Lumni Bay
Lumni Bay
1972
1973 a
a
Lumni Bay
Lumni Bay
m
1973 b
1974
Figure VI-1S LOCATION OF HERRING
SPAWN OBSERVED DURING SPAWNING
GROUND SURVEYS IN HALE PASSAGE
1972 - 1979
Source: Penttila, letter of November 20, 1979
-26 3-
-------
1975
1976 a
-------
Lumni Bay
*
Lumni Bay f
/ V
1977 b
1978 a
Lumni Bay
Lumni Bay
*
1978 b
1979
Figure VI-18 Continued
4 miles
-265-
-------
Extensive spawning surveys of Samish Bay were performed by FAO
in February and. March 1976. These revealed no spawn. The WDF
survey locations are summarized in Figure VI-19.
In Hale Passage, herring spawning activities occur from late
February, to early June (Penttila letter of November 1979).
Herring utilize the Samish Bay spawning grounds only during the
month of March (Trumble et al. 1977). Herring spawning is not
continuous throughout the season but occurs sporadically in
specific locations. As a result, an entire documented spawning
area may not be utilized each year.
Previous to the construction of Squalicum Mall marina and other
coastal changes, the shoreline west of Bellingham supported
surf smelt spawning grounds. Historically reported surf smelt
spawning grounds also existed along the shorelines of Fish
Point, Samish Island. Today this area is unproductive (Penttilia
letter of November 1979).
-266-
-------
Governors Point
Samish Bay
Fish Point
Edison Slough
Figure VI-19 LOCATION OF HERRING SPAWN
OBSERVED DURING SPAWNING GROUND
SURVEYS IN SAMISH BAY 1973-1977
Source; Penttila, letter Nov. 1970
1/fe miles
-267-
-------
P. WILDLIFE
The marine wildlife in the Bellingham and Samish Bay area is
categorized as (1) marine mammals and (2) marine birds. There
are only two marine mammals, the harbor seal and the killer
whale , that are considered to be year round residents in the
study area. Migratory bird species utilize both Bellingham
and Samish Bay areas for wintering and resting grounds. Nest-
ing locations in the area have been documented for only six
bird species.
1. Marine Mammals
The passage of the Marine Mammal Protection Act in 1972 initi-
ated research studies on marine mammal stocks of national
interest in the United States. One such study was conducted
by NOAA's Marine Mammal Division from November 1, 1977 to
October 31, 1978 in Northern Puget Sound and the Strait of Juan
de Fuca (Everitt et al. 1979). During the first year of the two
year study, monthly aerial and small boat surveys were conducted
in the area of interest. In addition to these surveys, the
resulting report (Everitt et al. 1979) contains an analysis of
existing literature and data, including mammal sightings.
Eight marine mammals representative of two mammalian categories
or groups are considered to be common (occur regularly) to the
Northern Puget Sound area (Table VI-18). The harbor seal/
killer whale, gray whale, and harbor porpoise are the only four
species that have been documented to occur in the Bellingham -
Samish area. The California and Northern sea lions, Minke
whale and Dall porpoise occur in waters immediately adjacent
to the study area. These species may possibly occur in Belling-
ham and Samish Bays on a rare or accidental basis. Further
marine mammalian studies are necessary to verify this assumption.
Only those marine mammals known to utilize the study area will
be discussed,, in the following section.
-268-
-------
Table VI-18. MARINE MAMMAL SPECIES COMMON TO NORTHERN
PUGET SOUND.
Pinniped (General term describing sea lions and seals)
Order: Carnivora
Family: Otariidae
California sea lion (Zalophus californianus)
Northern sea lion (Eumetopias jubatus)
F amily: Phocidae
* Harbor seal (Phoca vitulina richardsi)
Cetaceans (General term describing whales)
Order: Mysticeti (whalebone or baleen whales)
Family: Eschrichtiidae
* Gray Whale (Eschrichtius robustus)
Family: Balaenopteridae
Minke Whale (Balaenoptera acutorostrata)
Order: Oclontoceti (toothed whales)
Family: Delphinidae
Oall Porpoise (Phoceonoides dallii)
* Harbor Porpoise (Phocoena phocoena)
* Killer Whale (Orcinus orca)
* Species documented to occur in Bellinghaxn and Samish Bays.
Source: Everitt et al. 1979
-------
Documented Mammal Observations: Pinnipeds (sea lions and seals)
haul-out on land, becoming readily visible for aerial counts. Due
to the low abundance of migrating cetaceans (whales) in inland
Washington waters, distribution data is difficult to collect in
Northern Puget Sound. Accumulated whale sighting records maintained
by the Whale Hotline & Platforms of Opportunity Program (POP)
provide the majority of data in this field of study.
The harbor seal is a year round resident in Northern Puget
Sound. Haul-out areas for these seals are usually character-
ized as being isolated, having immediate access to deep water
or channels, and being near food sources (Everitt et al.1979).
Haul out sites are further divided into five categories. The
two represented in Bellingham and Samish Bays are areas having
(1) mudflats exposed at low tide and (2) anchored log booms
(Everitt et al. 1979, Brittell et al. 1975). There are 3
haul-out sites in the study area consistently used by harbor
seals (Figure VI-20).
The harbor seal is the only pinniped to breed and bear young in
Washington waters (Everitt et ajL. 19790 . During aerial survey
counts, pups were indicated separately from adults (Table VI-19).
In the study area, Samish Bay supports the largest population
of harbor seals.
The gray whale is a highly migratory species, usually occurring
singly or in pods of two to three. The eastern Pacific stock
spends the summer in the Arctic Ocean and Bering Sea and begins
a southern migration to Baja California and the Gulf of Cali-
fornia. The gray whale resides in this southern locale
throughout the winter before migrating north in late February
(Brittell et al. 1979). These north-south migrations are pri-
marily coastal, but occasionally the species occurs in
inland Washington waters. According to Whale Hotline records,
on June 24, 1978 one gray was sighted in Chuckanut Bay. During
the fall of the same year (June 24, 1978) another gray whale
was spotted in Hale Passage off Gooseberry Point (Figure VI-21,
Table VI-20 ) .
-27Q-
-------
, V
Strait of
Georgia
Lummi Bay
Areas Used
Consistently
Areas Used
Occasionally
Lohum :
tartan
tvmiionj
i m
Portaga
Portaga
Utnimi
Sinclair
Isl.
San Juan
Islands
SaJtingham
Chuckanut Bay\
Ptaaaant Bay
Eliza Isl.
Wildcat
Cava
j i
* 1
Vandovi
Isl.
Samisns
Isl.
Samiah Bay
Fidalgo
Bay
Anacortea*
Padllla Bay
0 100 200 400
50 150 300
thousands of tost
Figure VI-20
'HARBOR SEAL LOCATIONS IN BELLINGHAM AND SAMISH BAYS
OBSERVED DURING AERIAL SURVEY COUNTS? November 1,
1977 - October 31, 1978
Source: Everitt et al. 1978
-271-
-------
TableVI-19 . AERIAL SURVEY COUNTS OF HARBOR SEALS IN BELLINGHAM AND SAMISH BAYS.
(See Figure VI-20)
Station
Number
1977
Dec 8
1978
Jan 26
Jan 28
Feb 24
Mar 14
Aerial
Apr 25
Survey
May 23
Dates
May 25
Jun 27
Ju] 19
Jul 27
Aug 14
Aug 18
Sep 13
Oct 14
1
-
10
-
1
0
0
-
0
0
0
0
0
0
0
-
2
-
-
-
0
0
-
-
-
0
0
0
0
0
24
-
3
-
0
-
0
0
-
-
-
0
0
0
34 (6)
0
49 (1)
-
4
0
-
0
0
4
0
0
0
0
0
-
3
6 (1)
16
22
to
to
I
Key:
no survey
< ) pup8
Source: Everitt et al. 1979.
-------
NMksaefc ftinc
Strait of
Georgia
Lummi Bay , f LuRuwt
totflan
y*Mon
Baliingham
it
Portage B«yT\Portage
i es^v J \ isl.
~
Pt. Frances
Chuekanut
Plaaaant
1
UMnmi
I \ 1*1,
Eliza lsL
Wildcat Cova
Sinclair
Isl
San Juan
Islands
Samialt Bay
Samish
Isl.
Key
# Gray Whale
3k Harbor Porpoise
Fidalgo
Bay
Anacortas
0 100 200 400
/w/
50 150 300
W\/r i i i-"*^
thousands of feet
Figure VI-21 OBSERVATION LOCATIONS OF WHALES (CETACEANS) IN THE
BELLINGHAM - SAMISH BAY AREAS
Source: Everitt et al. 1979
-273-
-------
Table 20. OBSERVATIONS OF CETACEANS IN THE BELLINGHAM - SAMISH
BAY AREA
(See Figure VI-21)
Source: Everitt et al. 1979
Species
Date
Time
Number
Observed
Location
Gray Whale
6/24/78
0830-
1
Chuckanut Bay
0900
12/04/76
N/D
.1
Gooseberry Pt.
Harbor
7/06/65
N/D
1
Point Francis
Porpoise
7/10/65
N/D
1
Eliza Island
7/29/78
1825
2-4
Samish Bay
-274-
-------
There are four pods of killer whales that utilize all areas
of Puget Sound but are most commonly located in Northern Puget
Sound and the Strait of Juan de Fuca. These pods (J, K, L,
and 0) total 80 whales. The killer whale breeds year round,
with a peak period from May to July. In the Northern Hemi-
sphere most calving occurs in the autumn (Brittel et -al.
1975). Smaller marine mammals, sea birds, fish and cephala-
pods (molluscs such as squid, octopus etc.) are the main food
source for these whales.
The distribution of the four whale pods in inland Washington
waters is believed to be related to occurrence of prey
(Everitt et al. 1979). J Pod (18 whales) is the only year-
round resident pod in the area, located exclusively in the
Strait of Georgia, Puget Sound and eastern Strait of Juan de
Fuca (Figure Vl-22). K Pod (12 whales) and L Pod (40 to 45
whales) reside in inland Canadian waters and the west coast
of Vancouver Island, respectively. Both pods enter Washington
waters throughout the year. High occurrences of Pods J, K,
and L are documented in waters adjacent to Bellingham and
Samish Bays, but 0 Pod (4 whales) occurs in the study area
during August (Everitt et al. 1979). This appearance may relate
to the fall run of chinook in the Nooksack River.
The harbor porpoise is an inshore species located in coastal
waters, harbors, bays and the mouths of rivers. This year-
round resident of northern Puget Sound occurs in pairs and
schools of up to 200 individuals.(Brittel et al. 1975). The
occurrence of four to eight harbor porpoise in the Bellingham -
Samish Bay area is documented in Figure VI-21 and Table VI-2Q.
-------
Strait of Georgia
Bellingham
Victoria
Strait of Joatt tfa Fuc*
thousands off
0 260 520
130 390
Figure VI-22. MOVEMENTS OF "J" POD OF KILLER WHALES IN PUGET SOUND AND THE
STRAIT OF JUAN DE FOCA IN 1976-1977. The width of a line repre-
sents the relative number of occurrences in any one area. Dashed
lines represent hypothetical movements based on unconfirmed
-276
-------
2. Marine Birds
In Bellingham Bay there are 87 known marine bird species.
These are categorized as migratory (74 species), permanent
residents (5 species), or species populations which contain
both migratory and resident birds (8 species). Appendix Table 0 -l
shows the seasonal status for these birds (Webber 1975, Salo 1975,
Mathematical Sciences Northwest (MSN) 1977). An individual
species occurrence list for Samish Bay is not available in the
literature.
Information on the distribution and abundance of marine birds
occurring in Bellingham and Samish Bays has been retrieved from
studies conducted by WDG (Salo 1975), Huxley College of Environ-
mental Studies (Webber 1975), Mathematical Sciences Northwest,
Inc. (MSN 1977), and the Wildlife Science Group, University
of Washington (Manuwal et ail. 1979).
The WDG reviewed and compiled available Washington marine bird
data into a data retrieval system. The information is summar-
ized by Salo (1975). As part of a study of biological resources
in Bellingham Bay (Webber 1975), Terrence Wahl, a professional
ornithologist, provided information on the marine bird species
occurring in the Bay area. Mathematical Sciences Northwest (MSN)
(1977) conducted an analysis of existing data on 79 marine avian
(bird) species in Washington waters. Significant (critical and
important) biological areas for a species were determined according
to DOE guidelines.
From January 1, 1978 to December 31, 1978 the first year of a
two-year bird study was conducted in Northern Puget Sound.
Data on seasonal distribution, abundance, and species composi-
tion was collected by seven different census methods (Appendix
P ). The census results were used to calculate bird densities
and project seasonal species populations occurring oh the
shoreline and open waters of a given region. Breeding popu-
lations were also examined at this time.
-277-
-------
Bellingham Bay is located on a north-south flyway path for
western migratory birds. During the spring and fall migrations
both species diversity and abundance are high in Bellingham
Bay (Table Q-l) (Manuwal et al. 1979). These migra-
tory birds may utilize the study area to rest, feed, and breed,
or they may remain as seasonal residents. Individuals from 54
fall migrant species remain in Bellingham Bay throughout the
winter (Table Q-l). During this season marine bird populations
and densities are usually the highest for the year (Table
Q-l) (Manuwal et al. 1979). In the summer a variety of
non-breeding individuals may remain in Bellingham Bay. Only
two migratory species (Spotted sandpiper and Tufted puffin)
occur in the Bay area as a breeding summer resident (Table
Q-l). The remaining 26 migratory species use Bellingham Bay
as stop-over or resting grounds during their migration flights
(Table Q -1 ).
The major available bird habitats in Bellingham and Samish
bays include protected harbors, tidal flats, estuaries, and
marshes, undeveloped sandy beaches, rock islands and submerged
channels and reefs (Table VI-21). Gulls, grebes, cormorants,
loons, terns and murres use the open water in the Bays (Table
Q-l). Ducks, swans, coots and cranes usually seek the
sheltered areas of protected shorelines containing tidal flats,
lagoon, estuaries and marshes (Nooksack Delta and Samish Bay)
(Table Q - 1). Some ducks such as the Oldsquaw, Harlequin,
White-winged scoter, and Black scoter prefer open water habi-
tats (MSN 1977). The shorebirds perfer tidalflats and estuaries
(Nooksack Delta (MNS 1977). The sandy undeveloped beaches of
Samish Bay, Bellingham Bay, Portage Bay, Lummi Island, and
Portage Island also provide a favorable habitat for shorebirds
and gulls (Table Q-l). The only main channel in the study area,
Hale Pass, is widely used by gulls (Table Q - 1).
According to guildelines provided by DOE, Mathematical Sciences
Northwest defined 15 biologically significant marine bird areas
-273-
-------
Table VI-2 L AVAILABLE GEOGRAPHICAL BIRD HABITATS IN BELLINGHAM AND SAMISH BAYS
BIRD HABITATS*
(T.R. Hahl)
SITE OR AREA
Ocean Beaches, Sandy
focean Beaches, RockyJ
Tidal Flats
Estuaries, Small
Estuaries, Large j
1Salt Marsh
j Islands, Sandy
j Islands, Rocky
Major Entrance
Channels
Undeveloped Beaches,
- Sandy
r
Undeveloped Beaches,
Rocky
Sand Spits
Ocean Waters
Channels, Submerged
Reefs, etc.
Protected Harbors
Jetties
Rating **
Chuckanut Bay, Shorelines to Bellingham
X
X
X
XX
Nooksack Delta
X
X
X
X
X
xxx
Bellingham Bay
X
X
xxx
Portage Bay
X
X
X
X
x
Hales Pass
X
X
X
X
XX
Samish Bay
X
X
X
X
X
X
X
-
xxx
-
Source: MSN 1977.
•See key for description of Habitats (Appendix R)
**Ratinq x to xxxx - Subjective judgment of value of an area or feature on a state-wide basis.
Not quantitatively comparable area to areas (e.g. Bellingham Bay
(xxx) is more than three times as valuable as a one check (x) locations
(Portage Bay)). Rating dependent in part on amount of similar habitats
available, how intensive the habitat is tised and how unique is the
habitat area.
-------
in Bellingham and Samish Bays (Figures VI-23, VI-24, Table VI-22).
The individual significant areas for each species represent high
concentrations of winter residents, migratory species (spring and
fall) or nesting sites (Table VI-23). In addition to the Bald
Eagle and Great Blue Heron nesting sites identified by MSN, the
Wildlife Science Grouo (Manuwal et al. 1979) and WDG (Salo 1975)
located nesting grounds of four additional species (Mallard,
Tufted Puffin, Glaucous-winged Gull and Pigeon Guillemot)
(Figure VI-25).
-280-
-------
Table VI-22 KEY TO FIGURES VI-23 and VI-24 .
Figure Reference Significant Species *
A 2,-14
B 4, 5, 8, 9, 10, 11, 15
C 7
D 1
E 5
F 6
G 1, 3, 5, 7, 10
11, 12, 13, 15
* Refer to Table VI-23 for species identification.
-281-
-------
1000 2000
4000
500 1500 3000 yards
Beilingtiam
Luinim
Indian
Reservation
Bellingham
Bay
Post .<
Chuckanut
Bay
Lummf E*L
Governors
Point
Figure VI-23 BIOLOGICALLY SIGNIFICANT AREAS IN BELLINGHAM BAY
Source: MSN 1977
Refer to Tables VI-22, VI-23
-282-
-------
Strait of
Georgia
Gooseberry
Chuck amit
A Sinclair
1st
San Juan
Islands
FMaigo
100 200
50 150 300
thousands of foot
Figure VI-24 BIOLOGICALLY SIGNIFICANT AREAS IN SAMISH BAY
Source: MSN 1977
Refer to Tables VI-22, VI-23
-283-
-------
Table VI-23 BIOLOGICALLY SIGNIFICANT AREAS IN BELLINGHAM AND
SAMISH BAYS
Source: MSN 1977
Figure
Reference
Common Name
Scientific Name
1 Winter
Resident
Migration
Nesting
1
Black Brandt
Branta nigricans
•
•
2
Bufflehead
Bucephala albeola
•
3
Canvasback
Aythya valisinevia
• '
4
Dunlin
STolia atpina
•
5
Northern Bald Eagle
Saliaaetus teuaocephalus
•
6
Red-necked grebe
Podioeps grisegena
•
•
7
Western grebe
Aeahmo-phorous ocaident-
•
alis
8
Mew Gull
Looms eanus
«
•
9
Great Blue Heron
Apdea herodias
•
10
Mallard
Anas platyvhynohos
•
•
11
Pintail
Anas acuta
•
•
12
Black-bellied Plover
Squatapola aquatarola
•
•
13
Western Sandpiper
Ereunetes mxuri
•
14
Greater Scaup
Aythya marila
•
•
15
American Wigeon
Anas canerioana
•
¦
-284-
-------
NMfcucfc River
Lummi Bay , / tomwt
IiiidiM
.... vattoit
Gooseberry/:j
Bellingham Bay
BtMngham
Portage
rt. Frances
Inati Bay
liza IsL
Wildcat Cove
Sinclair
Xlsl.
San Juan
Islands
Vendovi
Isl
Legand
Glaucous
Samish Bay
Fish Pt.
Wlngad Gull
Mallard and
^ Tufted Pulfln
3|C Graat Blua
Pigeon Guillemot
• Bald Eagle
Fidalgo
Bay
Padilla Bay
100 200
50 150 300
thousands of test
Figure VI-25
DOCUMENTED NESTED SIGHTINGS
SAMISH BAYS
IN BELLINGHAM AND
Source: Salo 1978, MSN 1977
-285-
-------
REFERENCES
Ames,James. November 21, 1979. Personal communication to Kathy
Pazera, Biologist, Northwest Environmental Consultants,
Inc. (NEC).
Brittell, J. David, J.M. Brown, R.L. Eaton, C.A. Starika. 1975.
Marine Shoreline Fauna of Washington: A Status Survey.
Washington State Department of Game and Department of
Ecology. Vol. I and II. Appendix I and J.
CH2M Hill. 1974. Benthic and Water Quality Data in Bellingham
Bay. Taken for Georgia-Pacific Corporation and the City of
Bellingham.
CH2M Hill. April 1976. Bellingham Bay Monitoring Program;
A Report on Receiving Water and Sediment Quality in the
Vicinity of the Post Point Diffuser Outfall. Bellingham
Bay, Washington.
City of Bellingham. March 1978. Final Environmental Impact
Statement: Georgia-Pacific Bellingham Division. Gregory
Waddell Planning Director. 205 pp.
Evans, Daniel and D.W. Moos. 1976. 1975 Fisheries Statistical
Report, Department of Fisheries, State of Washington.
Everitt, R.D., C.H. Fiscus, and R.L. DeLong. January 1979.
Marine Mammals of Northern Puget Sound and the Strait of
Juan de Fuca. A Report on Investigations November 1, 1977-
October 31, 1978. National Marine Fisheries Service,
Seattle, Washington. Marine Ecosystem's Analysis Program.
191 p.
Geist, Richard. November 26, 1979. Personal communication to
Kathy Pazera, Biologist, NEC.
Goodwin, C.L. and W. Shaul. 1978a. Puget Sound Subtidal Hardshell
Clam Survey Data. Washington Department of Fisheries.
Progress Report No. 44, 92. pp.
Goodwin, C.L. and W. Shaul. May 1978b. Puget Sound Subtidal
Geoduck Survey Data, March 1977 - March 1978. Progress
Report No. 65. Washington State Dept. of Fisheries. 30 p.
Harman, Robert A. and John C. Serwold. 1975. Summary of Northern
Puget Sound Studies. For Northern Puget Sound Baseline Study.
Johnson, James.December 3, 1979. Personal communication to Kathy
Pazera, Biologist, NEC.
Manuwal, David A., Terence R. Wahl, and Steven M. Speich. Sept-
ember 1979. The Seasonal Distribution and Abundance of
Marine Bird Populations in the Strait of Juan de Fuca and
Northern Puget Sound in 197^. Marine Ecosystem's Analysis
Program, Boulder, Colorado. 391 pp.
-286-
-------
Mathematical Sciences Northwest, Inc. November 1977. Washington
Coastal Areas of Major Biological Significance. Baseline
Study Program. Washington State Dept. of Ecology. Appendix
G. 563 pp.
Meyer, John H. and Robert A. Adair. March 1978. Puget Sound
Herring Surveys, Including Observations of the Gulf of Georgia
Sac-Roe Fishery, 1375-W7.
Nelson, James M. et al. 1974. Mercury in the Benthos of Bellingham
Bay, Washington. Huxley College of Environmental Studies,
Bellingham, Washington. June 24, 1974 - September 13, 1974.
60 pp.
Orrell, Russell. December 3, 1979. Personal communication to
Kathy Pazera, Biologist, NEC.
Pattie, Brad and Wayne Gormley. January 1977. The 1975 Washing-
ton Trawl Landings by Pacific Marine Fishes Commission and
State Bottomfish Statistical Areas. Washington Dept. of
Fisheries Progress Report No. 11.
Pattie, Brad and Wayne Gormley. January 1978. The 1976 Washing-
ton Trawl Landings by Pacific Marine Fisheries Commission !
and State Bottomfish Statistical Areas. Washington Dept.
of Fisheries Progress Report No. 37.
Pattie, Brad. October 1978. The 1977 Washington Trawl Landings
by Pacific Marine Fisheries Commission and State Bottomfish
Statistical Areas Progress Report No. 76. Washington Dept.
of Fisheries.
Pentilia, D.E. November 20, 1979. Letter to Susan Hemingway,
Fisheries Biologist, NEC.
Phinney, Duane E. May 1977. 1977 Puget Sound Summer - Fall
Chinook Methodology: Escapement Estimates and Goals, Run
Size Forecasts, and In-Season Run Size.Updates. Technical
Report No. 29. 71 pp.
Poston, R.F. July 31, 1968. Letter to John Dunkak, General
Manager of Georgia-Pacific Corporation.
Puget Sound Task Force - Pacific Northwest River Basins Commission.
March 1970. Comprehensive Study of Water and Related Land
Resources, Puget Sound and Adjacent Waters, State of Washing-
ton. Appendix XI. Fish and Wildlife.
Rasch, Tony and Robert Foster. May 1978. Hatchery Returns and
Spawning Data for Puget Sound, 1960 - 1971TI Progress Report
No. 59. Washington State Department of Fisheries. 263 pp.
-287-
-------
Ross, J.R.P. and K.S. McCain. 1976. "Schizoporella unicornis
(ectoprocta) in Coastal Waters of Northwestern United States
and Canada". Northwest Science. Vol. 50, No. 3, pp. 160-171.
Salo, Leo J. September 1975. A Baseline Survey of Significant
Marine Birds in Washington State. Prepared for the Washing-
ton State Oil Baseline Program. Appendix H. 417 pp.
Scott, W.B. 1973. Recent Benthic Foraininifera from Samish
and Padilla Bays, WA. M.S. Thesis, Westerns Washington State
College. 20 pp. J
Scott, W.B. and E.J. Crossman. 1975. Freshwater Fishes of"
Canada. Fisheries Research Board of Canada, Ottawa. Bulletin
No. 184, 966 pp.
Sjolseth, D.E., E.O. Salo and M. Katz. 1970. Effect of Water
Quality in Bellingham Bay on Juvenile Salmon. Presented
at the 5th International Water Pollution Research Conference
July - August 1970. Proceedings Published by Pergamon
Press Ltd. Spring 1971.
Smith, Gary F. 1976. A Quantitative Sampling Program of Benthic
Communities in Nearshore Subtidal Areas Within the Rosario
Strait Region of Northern Pu^et Sound, Washington State.
Huxley College, Western Washington University. 105 pp.
Sternburg, Richard W. 1967. "Recent Sediments in Bellingham Bay,
Washington". Northwest Science 41(2):63-79.
Tollefson, Roger. 1961. Summary Of Existing Hydrographic Data -
North Puget Sound 1953-1961.
Tollefson, Roger. 1962. Basic Biological Productivity - Belling-
ham Bay, March 1959 - July 1961. 128 pp.
Trumble, Robert, Dan Pentilla, Dwane Day, Pat McAllister, John
Boeltner, Robert Adair and Paul Wares. July 1977. Results
of Herring Spawning Ground Surveys in Puget Sound, 1975 ~~
and 1£76. Progress Report No. 21.
Tyler, Richard W. May 25, 1964. Distribution and Migration of
Young Salmon in Bellingham Bay, Washington . Fisheries
Research Institute Circular No. 212, University of Washington,
College of Fisheries. 26 pp.
U.S. Department of Interior (USDI). 1967. Pollution Effects of
Pulp and Paper Mill Wastes in Puget SouncT A Report on
studies conducted by the Washington State Enforcement Project.
FWPCA and WPCC, Portland, Oregon and Olympia, Washington.
474 pp.
-288-
-------
Ward, Dale, R. Robison and A. Palmen. 1964. "1963 Fisheries
Statistical Report" IN: Dept. of Fisheries 73rd Annual
Report. Washington State Dept. of Fisheries.
Washington State Department of Game. 1962-1977. Summary of
Steelhead Catch Returns.
Webber> H.H. 1975. The Bellingham Bay Estuary, A Natural History
Study. U.S. Fish and Wildlife Service. 92 pp.
Webber, H.H. April 1977. Bellingham Bay Literature Survey.
Huxley College of Environmental Studies. Bellingham, Washing-
ton. 52 pp. Western Washington University.
Webber, H.H. June 1978. Studies on Intertidal and Subtidal Benthos,
Fish and Water Quality in Bellingham. Huxley College,
Western Washington University, Bellingham, Washington. 78 pp.
Williams, R.W., Richard M. Laramie, and James J. Ames. November
1975. A Catalog of Washington Streams and Salmon Utilization.
Vol 1: Puget Sound Region.
Withier, I.L. 1966. Variability of Life History Characteristics *
of Steelhead Trout (Salmo gairdneri) Along the Pacific Coast*
of Canada. Journal Fisheries Research Board of Canada
23(3): 365-393.
Zillgis, Gordon. November 21, 1979. Personal communication
to Kathy Pazera, Biologist, NEC.
-289-
-------
VII. ECOLOGICAL EFFECTS
A. OVERVIEW
Ecologically, Bellingham Bay is an estuary which forms a mixing
zone for freshwater flows from two rivers. At the north end,
the Nooksack River adds-a mean flow of 104 cubic meters per
second (m3/sec) to the 3535 - 4063 cubic meter volume of tidal
marine waters in the Bellingham - Samish Bay system. To the
south, the Samish River adds a considerably smaller flow of
6.8 m3/sec. The effect of these flows is to create two freshwater
lenses in marine waters which otherwise range up to 25 - 30 ppt
salinity. The Nooksack lens dominates the Bay, particularly
the northern portion near Bellingham.
The presence of both saline and brackish waters provides habitats'
for several assemblages of biological species, each adapted to
particular salinity conditions. The effects of wind and currents
on the distribution of fresher water combined with the presence
of industrial effluents from the Georgia-Pacific pulpmill and other
sources cause shifts of distribution of these biological popula-
tions. In general, however, enough studies exist over the past
two decades to deduce major populations, their distributions and
some information concerning biological diversity. Little infor-
mation is available on production feeding habits and trophic
relations in the ecosystem.
Primary production in Bellingham Bay is high in comparison with
other marine waters (Riley 1972, Rhyther and Yentsch 1957). This
is thought to be largely due to continual replenishment of
phytoplankton populations from the Nooksack River and from incoming
tides. The high productivity was found to be reduced in the
northeast corner of Bellingham Bay by SSL concentrations (USDI
1967). SSL levels remained at potentially deleterious levels even
after installation of primary treatment in 1973 (USDI 1967,
CH2M Hill 1974 > .
-290-
-------
The high primary productivity in most of Bellingham Bay provides
a basis for a relatively abundant and diverse assemblage of
consumer organisms (enumerated in Chapter VI). Zooplankton
are of high abundances and diversities. The particularly high
concentrations of zooplankton and invertebrates at depths over
20 feet indicates a strongly functioning benthic community at
depths where the majority of the mill effluent does not penetrate.
This may also indicate that Bellingham Bay zooplankton are not
as well adapted to the fresher surface waters.
Eggs and larvae of flounder and sole are generally distributed on
the water surface and are found to be physiologically damaged by
SSL or associated effluents (USDI 1967). Effects on other organ-
isms are not well-documented for Bellingham Bay; however, both
direct effects and effects transmitted through the food chain
have been documented for many of the organisms present in Bellingf
ham Bay (see below).
Diversity of organisms has been found to fall off rapidly for
sampling stations near Georgia-Pacific's original nearshore
outfalls during the period following primary but preceeding sec-
ondary treatment (Nelson et al. 1974, CH2M Hill 1974, Webber 1978).
The drastic reductions in invertebrate diversities (1.5 - 2.0, outer
harbor to 0.0 - 0.7 in Whatcom Waterway) indicate that many species
cannot meet basic survival requirements in water affected by the
discharges of pulp effluents.
In the following sections, ecological effects of pulpmill effluents
are discussed in relation to trophic structure, damage mechanisms
of effluents, and overall ecosystem indices. The description
of the ecosystem is valid for the period preceeding the instal-
lation of secondary treatment by Georgia-Pacific, since
insufficient time has elapsed since June 1979 to note significant
biological changes.
-291-
-------
B. TROPHIC STRUCTURE
Food webs and trophic pathways in Bellingham Bay have not been
documented in the literature. The best current information is
contained in recent baseline studies for NOAA and Washington
Department of Ecology (DOE) (Simenstad, personal communication 1980).
This data has been synthesized from fish trawls and stomach
content analyses conducted by the University of Washington, as
well as invertebrate research at Western Washington University.
The research has been conducted on several areas near Bellingham
Bay, including Lumiiti Bay, San Juan Islands and Fidalgo Bay.
These food webs are expected to correspond roughly to conditions
in Bellingham Bay, except where industrial pollutants or the
Nooksack freshwater plume are dominant.
Diagrams of food webs near Bellingham Bay show a high complexity
which corresponds well with the comparatively large number of geqera
in Bellingham Bay (Table VII-1). Food webs for mud and eelgras^
substrates are shown in Figure VII-1 and VII-2. It should be
noted that areas containing eelgrass are the most diverse since
they provide protective habitat for many species. Table VII-2
shows the degree of similarity between the species found in
mud/eelgrass habitats found by simenstad near Bellingham Bay
(Wescott Bay, San Juans) and the actual biota of the Bay itself.
The major difference is the presence of migrating salmon and
trout in Bellingham Bay which are not included in Simenstad's
study area. This may alter food web characteristics in Belling-
ham Bay substantially from those shown in Figures VII-1 and
VII-2.
The bottom habitats of Bellingham Bay are primarily mud or
muddy silt. Eelgrass beds occur in several areas including
Chuckanut Bay, Portage and Eliza Islands. Known sand and
gravel habitats are limited to a sand trench east of Eliza
Island and a sand-gravel area around Post Point. Silt from the
Nooksack River overlies the bottom muds in the delta area.
-292-
-------
Table VII-1. THE MINIMUM OF KNOWN MARINE GENERA AT PORT TOWNS END, PORT ANGELES AND
BELLINGHAM BAY, WASHINGTON
Number of Genera
Group Subgroup Port Townsend Port Angeles Bellingham Bay
Macroalgae Brown algae unknown unknown 1
Red algae M " >1
Green algae " " 2
Phytoplankton Blue-green algae " " unknown
Euglenoids ¦* " "
Diatoms " 32
Dinoglagellates " unknown "
Tintinnids " " "
Ciliates " " "
Flagellates ** " "
Mlcroflagellates " " *
Zooplankton Ichthyoplankton 1 8-15 >1
Other Zooplankton 8 23 69
Shellfish Subtidal Hardshell Clams 3 3 3
Intertidal Clams unknown unknown 3
Geoducks 111
Invertebrates Mo Husks 23 unknown 82
Starfish 1 2 unknown
Crustaceans 24 - 28 unknown
Segmented worms 18 11 78
Roundworms unknown unknown 3
Jellyfish and sea anemones " 5 unknown
Comb jellies " 15
Fish Marine 42 89 66
Anadromous 2 7 9
Marine Mammals Seals and Sealions 2 5 1
Dolphins, Porpoises and Whales 4 14 3
Otter unknown 1 unknown
Marine Birds Gulls and Terns unknown 10 13
Cormorants "33
Ducks 8 20 26
Geese and Swans unknown 3 2
Loons i» 3 4
Herons ~ 1 1
Grebes unknown 4 5
Continued
-------
Table VII-1, Page 2
Number of Genera
Group
Subgroup
Port Townsend
Port Angeles
Bellingham Bay
Marine Birds
Sandpipers and other shorebirds
unknown
12
15
(Cont.)
Rails
••
1
1
Plovers
H
3
4
Cranes
It
unknown
1
Alcids
M
4
5
Phalaropes
II
1
1.
Jaegers
II
unknown
1
Kingfishers
II
1
1
Eagles, Hawks and Falcons
1
1
4
-------
Great Blu*
Heron
Saddleback
Gunnel
Starry
Flounder
IJuv.1
English
Sole
IJuv.l
Snake
Prick leback
Buffalo
Sculpln
Fish
llnc.Pac.
Herring.
Shiner R
Hlppolytid
Shrimp
Crangonld and
Penaeld Shrimp
Brachyuran
Crabs
Saltmarsh Plants
and Eelgrass
Macrophytlc Algae
line. Ul¥« species I
Detritus
Figure VII-1. SHALLOW SUBLITTORAL FOOD HEB IN
MUO/EELGRASS HABITAT NEAR BELLINGIIAH
BAY (Wescott Bay, Spring Food Web,
San Juan Islands)
Source: Simenstad (1979 personal conrauni-
cation) and Simenstad et al. 1979 *
Relative Importance
ol
Food Web Linkages
Primary 175-100% ol total I.R.I.I
Secondary 150-75% ol total I.R.I.I
Tertiary 125^50% ol total I.R.I.I
Incidental 15-25% ol total I.R.I.I
-------
I
ro
10
a\
t
Mallard,
Pintail.
Whlmbrel,
Northern Shovaler,
Western Sandpiper
Long-Billed,
Short-Billed
Dowltchers
*
Great Blue
Heron
\
r~H
Tldepool
Sculpin
Padded
Sculpin
Sharpnose
Sculpin
Tldepool _
SHverspotted
Sculpin
Starry
Flounder
V
Spiny
Lumpsucker
Buffalo
Sculpin
Sturgeon
Snake
Prlckleback
English
Sole
IJuv.l
Staghorn
Sculpin
Fish
line. Pac.
\ Si Poacher IJk
Herring, J\ 1/
Shiner R * \ 3K
ZjSx Vil-
li " ' V /.
Polychaete I /1
Annelida I / I
' P /1 U.I.
Hyperlld
Amphlpods
Harpactlcoid
Copepoda
Qammarld
Amphlpods
Bivalves
linc.slphonsl
r.
Crangonld and
Penaeld Shrimp
Valvlleran
Isopods
Copepods
Macrocytic
/
spec.1
Sail marsh Plants
and Eelgrass
Detritus r-^
| Phy toplankton [
Figure VII -2 SHALLOW SUBLITTORAL FOOD WEB IN MUD/
EELGRASS HABITAT NEAR BELLINGHAM BAY (Wescott Bay,
Fall Food Web, San Juan Islands)
Source: Simenstad (1979 personal communication
and Simenstad et al. 1979
Relative Importance
of
Food Web Linkages
Primary 175-100* of total I.R.I.I
Secondary 150-75% of total I.R.I.I
Tertiary 125-50% of total I.R.I.I
Incidental 15-25% of tolal I.R.I.I
-------
Table VII-2 DEGREE OF OVERLAP OF SPECIES GROUPS BETWEEN BELLINGHAM BAY AND NEARBY
AREAS WITH KNOWN TROPHIC STRUCTURES
Area
Habitat
Number of Bellingham
Bay Species Found*
Percent overlap with
Bellingham Bay
San Juan Islands
Deadman Bay
Eagle Cove
Westcott Bay
Gravel
Sand/eelgrass
Mud/eelgrass
41
36
39
82%
92%
86%
Cherry Point
Legoe Bay
Gravel
42
85%
Anacortes
Guemes South
Fidalgo Bay
Gravel
Mud/eelgrass
42
43
82%
87%
*
see Chapter VI for Bellingham Bay species.
Derived from: Simenstad, C.A. unpublished data; Simenstad, MESA Food Web Report, In Press.
-------
The inner harbor is modified by the presence of wood chips, and
fibers from Georgia-Pacific, as well as debris from other dis-
charges (Figure VII-3). Beach types include both rock-cobble
and sand-gravel scattered somewhat randomly throughout the Bay.
Webber (1977) discusses benthic and beach habitats in more
detail.
Effects of sulfite and bleached sulfite mill effluents have been
found to include loss of productivity in phytoplankton (Eloranta
and Eloranta 1974, Moore and Love 1977) and death or reduced
feeding in fishrcrustaceans and invertebrates (Hutchins 1979).
Other organisms are potentially affected through direct or food
chain effects including zooplankton, ichthyplankton (USDI 1967),
shellfish and marine birds.
Figures VII-4 and VII-5 show food webs based on typical mud-
eelgrass habitat and deepwater habitat typical of the marine
waters near Bellingham Bay. The shaded and marked organism
groups show those likely affected either directly based on known
feeding patterns or the literature on sulfite mill effluent.
Biological effects of sulfite effluent are not as well known as
are those of the kraft process. Due to this lack of information,
Figure VIII-4 also includes known effects of other effluent
types (kraft) which have been more thoroughly studied. Ecologi-
cal toxicity of effluent components such as heavy metals, chlor-
inated hydrocarbons, terpenes, phenols and resin acids have
been documented for sulfite effluent, even though studies of non-
salmonid organisms are rare (Becker and Thatcher 1973, Easty et
al. 1978, Hutchins 1979).
As toxic compounds are taken up by organisms and later trans-
mitted to other elements of the food chain, toxic effects may
increase due to:
• cumulative buildup in an organism
• synergistic effects in combination with other toxins
• accumulation and concentration in higher levels of
the food web
The mechanisms of these effects have not been well studied for
pulpmill effluents; however, studies of PCB's and heavy metals
-298-
-------
9 1000 2000 4000
500 1500 3000 yards
tiooksack fifewr
•Legend •
Eelgrass Beds
Silt
All Other Habitats
Inon-mudl
Bellingham
.
Lumsni
India*
feneration
mud
Portage
Bay
Liamra t$|.
wood ehlBB A fibre
Bellingham
Bay
mud
^PIOaKi
{ Pt.
—nd > gravi
mud
Eliza Island
Jk f
t sand
At\
$1
1
II
M
4
Chuckanut
Bay
Pleasant
Governors
Point
Figure VII-3. HABITAT TYPES IN BELLINGHAM BAY (Primary habitat
is mud - others are as marked)
Source: Webber 1978
-299-
-------
Figure VII -4
EFFLUENTS
SPECIES KNOWN TO BE DETRIMENTALLY AFFECTED BY SULFITE OR OTHER MILL
KjfeddedW IST
jpculpln I |p6
M
Mallard,
Plnlall,
Whlmbrel,
l^brtharn Shovelar,
Western Sandpiper
\ong-Bllled,
Short-Billed
/6owltchera
real Blue
Heron
Idepool
Bay
Wpallah
Tldepool
Snallfiah
culpln
Sllvarspolled
Sculpln
V/
\
\
R|»r#»««
y ^ >"^IPoachar
Spiny
umpauckar
nallsh
Icklebackl j j
flhorn
culpln
§yunlcatas|
yparlld
mphlpods
Harpacllcold
Copapoda
Polychaete
CrangonM S3
pantatd Stuimp
V.
Valvlteran
iaopod«|-
pepods
/
Saltmarsh Plants
and Eetarass
n-
i
Directly allaclad
laulfltel
Indirectly affected
I sulf ite I
Directly affected
lother pulp affluental
Indirectly affected
lother pulp effluentsl
Source: Simenstad (1979 personal
communication) and Simenstad et
al. 1979
Relative Importance
of
Food Web Llnkagea
Primary 175-100% of total I.R.I.I
Secondary 150-75% of total I.R.I.I
Tertiary |2S-S0% of total I.R.I.I
Incidental 15-25% of total I.R.I.I
-------
Figure
WITH
VII -5
SPECIES
NERITIC FOOD WEB NEAR BELLINGHAM BAY (Anacortes, Summer Food Web)
KNOWN TO BE DETRIMENTALLY AFFECTED BY SULFITE OR OTHER MILL EFFLUENTS
Chum
Salmon
ladult;
nonfeedlngl
Anadromoua
Rainbow Trout
ladult;
nonfeedlngl
/
1
1
Pink
/
/
Chinook
Coho
1
1
i
. Salmon
ladult;
nonfeedlngl
Salmon
ladult;
nonfeedlngl
Salmon
ladult;
nonfeedlngl
ftftilMMI
Pink
Salmon
IJuv.1
Mmw'
®JV
dpota
culpln
aclflc sand
Lane*
Myslds I
l^uphauslida
Harpacllcold
Copapods
Dipteran '
Nyperlld
mphlpods
J
opepods
\ |Cumaceana
lanktonlc
Idarlans
Oatracoda
sopoda
Diractly affactad
~ Isulfltal
_ indirectly affactad
Isulfltal
Source: Simenstad (1979 person-
al communication) and Simenstad
et al.1979
Ralattva Importance
of
Food Wab Linkages
Primary 176-100% of total I.R.I.I
Secondary .150-75X . of total I.R.I.I
Tartlary 125-50 X of total I.R.I.I
Incidental 15-25% of total I.R.I.I
-------
related to pulpraill components have shown considerable affinity
for cumulative and food chain buildup (Harris 1971, Macek and
Korn 1970, Lowman et al_. 1971) . Thus both bioaccumulation of
toxicants and reduced abundance of food organisms can be
expected to most severely affect top food web predators in-
cluding man.
C. DAMAGE MECHANISMS
Ecological damage occurs basically at an organismic or species
level. This damage then causes shifts in established ecological
balances including changes in community structure, species
diversity, and productivity. In this subsection, damage mech-
anisms are discussed in terms of organismic effects. Ecosystem.,
implications are discussed in Section VII.0. below.
Bioassay tests are designed to detect acute, high level damage
from pollutants which causes organismic death or disability
following a relatively short exposure (e.g. 96-hour). Other,
more subtle effects of pollutants and toxicants may exist. These
effects may cause:
• direct death of the organism over a long time
period
• sublethal abnormalities (morphological or physio-
logical) which decrease survival chances
• behavioral modifications which cause inability to
complete critical lifecycle stages
• genetic alterations
• increased susceptibility to other stresses
• impacts on organisms higher in the food chain
Any of these mechanisms may cause severe long-term damage in the
survival ability of the species as a whole.
Not all organism deaths can be expected to be evident during a
96-hour bioassay. Early studies with kraft mill effluent (Wash-
ington Department of Fisheries I960) showed that the majority of
-302
-------
fish (Oncorhyrnchus kisutch) tested often survived a 96-hour
exposure to the effluent levels of 6 percent or less and succumbed
after exposure of 5 - 18 days. In some cases, the major die-off
occurred during the fifth or sixth day. In other instances, the
organism may be affected more slowly than found in these tests,
possibly completing a significant part of its lifecycle before
dying. The only methods of determining such long term effects would
be long term.field bioassays.
Physiological or morphological abnormalities induced by exposure
to effluents can potentially decrease the probability of an
organism's survival in its natural habitat. Studies of lethal
effects of sulfite mill effluent (without secondary treatment)
have been found for salmon and trout (Rosehart et al. 1979, Wilson
and Chappell 1973, Kondo et al. 1973, Wilson 1972). Physiological
changes induced by sulfite mill effluent which do not cause
immediate death have been found to include:
• lower growth rates (Seppovara and Hymninen 1970)
• reduced blood value (Seppovara 1973)
• abnormal larval development (Woelke 1960)
• altered oxygen uptake (Gazdziauskaite 1971 a,b)
• reduced swimming activity (Seppovara 1973)
Other metabolic and morphological disturbances have been noted
for other types of mill effluent, but are not covered in the
sparse literature on sulfite effluents.
Behavioral changes in fish due to pulpmill effluents have been
documented in the laboratory (Hutchins 1979); however, these
have been limited to avoidance behavior. No information is avail-
able on the effects that mill effluent may have on migrating
pathways of juveniles or spawning returns of adult anadromous
fish. Subtle chemical changes are known to inhibit the ability
of juvenile fish to adapt to marine waters, and it is also
possible that exposure to toxic substances may upset the delicate
homing mechanism which contributes to succiessful anadromous fish
spawning.
-303-
-------
Genetic changes are the most subtle effects of toxic substances,
often being essentially undetectable in the organism itself and
sometimes masked in succeeding generations. However, genetic
alteration can affect reproductive success and survival of
juvenile organisms, as well as being transmitted to succeeding
generations of organisms. Ferguson (1970) has shown for toxic
pesticides that genetic changes cause resistant genes to become
dominant, often making the species less well-adapted for normal
environmental factors.
Low level, chronic exposure to toxicants has been shown to
result in cumulative buildup within the organism which can cause
death or sublethal effects after an extended period of time
(WDP 1960). A toxicant can also result in no overt, observable
reaction in an organism, while operating on a subtle, invisible
level. This may cause the organism to be more susceptible to
natural stress factors in its environment or to other toxicants^
in a synergistic reaction (Ferguson 1970, Hutchins 1979). Such
effects have not been substantially studied in the experimental
literature.
D. ECOSYSTEM EFFECTS
Bellingham Bay has been the site of the Georgia-Pacific pulpraill
and numerous other industrial and domestic pollution sources
for over half a century. There is no baseline data from which
to deduce the natural state of the bay. Nevertheless, patterns
exist which clearly demonstrate that both primary treated and
untreated mill effluent have affected the biota in portions of
the bay. The case for this argument is strongest, of course,
in the vicinity near the mill. There is clear evidence from
Chapter VI above that:
• primary productivity is lowered near the mill
• secondary zooplankton productivity is lowest in surface
layers which contain the bulk of effluent
-304-
-------
• secondary productivity is lowered through adverse
effects on larval and juvenile fish
• ecosystem diversity is drastically affected near
Whatcom Waterway
These factors are only the acute indicators of ecosystem stress
from sulfite mill effluents. Oceanographic patterns indicate
that effluent typically diffuses throughout the upper bay with
a general southeasterly trajectory. This pattern coincides with
locations of fish migration, oyster beds and areas used by marine
mammals and birds, as the effluent reaches the western islands
(Eliza, Lumrai) and the lower areas of the east bayshore. There
is a good probability that the chronic buildup of effluent over
long periods of time may affect the- stability of resiliency of
these ecological resources.
Through its action on various organisms in the food web, sulfite
mill effluent may cause a combination of lethal and sublethal
effects in organims which shift the foodweb balance. The elimina
tion of lower trophic level organisms can potentially eliminate
critical pathways causing reductions of organism abundances in
upper positions in the food web.
E. SUMMARY
It should be pointed out that while the above discussion is
somewhat speculative with regard to the exact mechanisms and the
severity of damage resulting from pulpmill effluents, the ecolo-
gical literature supports and confirms the potential for such
damage. Numerous other classes of biological toxicants (e.g.
heavy metals, PCB's) have been found to exhibit these mechanisms
in biological organisms individually and in overall ecological
systems.
Pulpmill effluents have historically been studied from a direct,
acute cause-effect standpoint. Little or no scientific work has
focused on the subtler implications of those effects.
-305-
-------
REFERENCES
Becker, c.D., and T.O. Thatcher. 1973. Toxicity of Power Plant
Chemicals to Aquatic Life. United States Atomic Energy
Commission. June 1973.
CH2M Hill. 1974. Benthic and Water Quality Data in Bellinqfram
Bay. Taken for Georgia-Pacific Corporation and the City of
Bellingham.
Easty, D.B., B.A. Wabers and L.G. Borchardt. 1978. Removal of
Wood Derived Toxic Compounds from Pulp and Paper Mill Effluents
by Waste Treatment Processes. TAPPI Conference Proceedings,
1978. pp. 37-43.
Eloranta, V. and P. Eloranta. 1974. "Influence of Effluent of
Sulfite Cellulose Factory on Algae in Cultures and Receiving
Waters." Vatten 1 36-48.
Ferguson, D.E. 1970. "The Effects of Pesticides on Fish: Changing
Patterns of Speciation and Distribution". IN: The Biological
Impact of Pesticides in the Environment (J.W. Gellet (ed.)),
Proc. Symp. Environ. Hlth. Sci. Series No. 1, p 83-86.
Gazdziauskaite, I.B. 1971a. "Effects of Effluents from the
Sovetsk and Neman Mills on the Biology of Pontogammarus
robustoides." (1) Vitality. (2) Respiration Intensity. Liet>
TSR Mokslu. Adad. Darbai Ser. C. No. 2:93. (Ab. Bull. Paper
Chem. 43:10694)
Gazdziauskaite, I.B. 1971b. "Effects of Effluents from Sovetsk
and Neman Sulfite Pulp and Paper Mills on the Fertility of
Pontogammarus robustoides (Grimm) sars". Rybokhoz. Ishuch.
Vnutr. Vodoemov No. 6:29-31. (Ab. Bull. Inst. Paper Chem.
43:3026).
Harris, Robert C-. July 1971. "Ecological Implications of
Mercury Pollution in Aquatic Systems." Biological Conserva-
tion Vol. 3, No. 4. pp 279-283.
Hutchins, F.E. February 1979. Toxicity of Pulp and Paper Mill
Effluent: A Literature Review" Corvallis Environmental
Research Laboratory; EPA-600/3-79-013.
Kondo, K. Sameshima and T. Kondo. 1973. Spent Semi-chemical
Pulping Liquor(3)Toxicity Characteristics of SCP Spent Liquor
and Reduction of its Toxicity. Japan TAPPI 10:476.
Eowman, G.G., T.R. Rice and F.A. Richards. 1971. "Accumulation
and Redistribution of Radionuclides by Marine Organisms."
IN: Radioactivity in the Marine Environment. National Academy
57 Sciences, Washington D.C. pp 161-199.
Macek, K.J. and S. Korn. 1970. "Significance of the Food-Chain
in DDT by Fish." J. Fish. Res. Bd. Canada 27(8):1496-1498.
30 6
-------
Moore, J.E. and R.J. Love. 1977. "Effects of a Pulp and Paper
Mill Effluent on the Productivity of Periphyton and Phyto-
plankton. " Journal Fish. Res. Board Canada. 34:856-862.
Nelson, James M. et al. 1974. Mercury in the Benthos of
Bellingham Bay, Washington. Huxley college of Environmental
Studies, Bellingham, Washington. June 24, 1974 - September
13, 1974. 60 pp.
Rhyther, J.H. and C.S. Yentsch. 1957. "The Estimation of
Phytoplankton Production in the Ocean from Chlorphyll and
Light Data." Limnology and Oceanography 3:281-286.
Riley, G.A. 1972. "Factors Controlling Phytoplankton Populations
on Georges Bank." IN: Readings in Aquatic Ecology: R.F.
Ford and M.E. Hazen~Teds.). W»B. Sanders Company, Philadelphia,
PA.
Rosehart, R.G., G.W. Ozburn and R. Mettinen. June 1974. "Origins
of Toxicity in Sulphite Pulping." Pulp and Paper Magazine
of Canada. 75(6): 63-66.
Seppovaara, 0. 1973. "The Toxicity of the Sulfate Pulp Bleaching
Effluents." Paperi Ja Puu. 55:713. (Ab. Bull. Inst. Paper
Chem. 44:109lUTT
Seppovaara, 0. and P. Hynninen. 1970. "On the Toxicity of Sulfate*
Mill Condensates." Paperi Ja Puu. 52:11 (Ab. Bull. Inst.
Paper Chem. 41:487).
Simenstad , Charles A. March 1980. Personal communication to
G. Bradford Shea, Ecologist, NEC.
Simenstad, c.A., B.S. Miller, C.F. Nyblade, K. Thornburgh, and
L.J. Bledsoe. September 1979. Food Web Relationships of
Northern Puget Sound and the Strait of Juan de Fuca. Prepared
for MESA Puget Sound Project.
United States Department of the Interior. 1967. Pollution Effects
of Pulp and Paper Mill Wastes in Puget Sound. A Report on
studies conducted by the Washington State Enforcement Project.
FWPCA and WPCC, Portland, Oregon and Olympia, Washington.
474 pp.
Washington Department of Fisheries. 1960. "Toxic Effects of
Organic and Inorganic Pollutants on Young Salmon and Trout."
Research Bulletin No. 5. Olympia, Washington. 252 pp.
Webber, H.H. April 1977. Bellingham Bay Literature Survey.
Huxley College of Environmental Studies. Bellingham, Washing-
ton. 52 pp. Western Washington University.
Webber, H.H. JUne 1978. Studies on Intertidal and Subtidal
Benthos, Fish and Water Quality in Bellingham. Huxley College,
Western Washington University, Bellingham, Washington. 78 pp.
Wilson, R.C.H. 1972. "Acute Toxicity of Spent Sulfite Liquor
to Atlantic Salmon (Salmo salar)." J. Fish. Res. Board Canada
29:1225-1228.
-307-
-------
Wilson, M.A. and C.I. Chappell. 1973. Reduction of Toxicity
of Sulfite Effluents. CPAR Report No. 49-2. Canadian For-
estry Service, Ottawa, Ontario.
Woelke, C.E. 1960. "Effects of Sulfite Waste Liquor on the
Normal Development of Pacific Oyster (Crassostrea gigas)
larvae". Washington Dept. of Fisheries Research Health,
20, pp. 45-51.
-308-
-------
VIII. ANALYSIS AND RESULTS
This chapter presents analyses carried out on Bellingham Bay
area data by the project team (report authors). The analysis
has been based on data pertaining to oceanographic dynamics,
water quality, toxicity, biology and ecology presented in
Chapters III - VII. Oceanographic analysis has been carried
out by Evans-Hamilton Inc., toxicity analysis by Dr. Quentin J.
Stober and NEC Staff, and water quality, biological and eco-
logical analysis by Northwest Environmental Consultants, Inc.
A. OCEANOGRAPHIC DYNAMICS
In this section, analyses of flow characteristics, water pro-
perties and dilution are discussed. The analysis focuses on
the Georgia-Pacific mill (hereafter GP), even though the Scott
Paper Mill (hereafter SP) also contributed effluents to the
Rosario Appendage (hereafter RA) system prior to 1978.
1. Mean Current Flows
The plan view of shallow and deep currents is shown in Figure
VIII-1. The records used to construct this figure were ob-
tained at varibus times using different equipment; for perspec-
tive the results have been combined in a single plan view.
Figure Vlll-lb consists of mean currents obtained in the depth
range of 2.5 - 6.5 m; Figure VIII-lc consists of current
measurements taken in the depth range 20 - 25 m ; and Figure
VIII-Id in the range of 35.9 - 98 m.
The plan view of net currents (Figure VIII-1) indicates that
the net southward flow which enters the northern end of Rosario
Strait is divided into two major streams in the vicinity of the
area circumscribed by Lawrence Point to Sinclair Island to
Lummi Island. One major stream turns clockwise through approxi-
mately 90° to continue southward along the main axis of Rosario
-309-
-------
I
u
»-*
0
1
ez* 30'
• ** •
m
BZ* SO*
122* 30*
f • 20cm »H
122* 90'
A. CURRENT METER SITES
B. 2.5 - 6.5 m depths
Figure VIII-1 MEAN CURRENT PATTERNS IN THE ROSARIO APPENDAGE
Sources: Collias 1971 (square), USCGS (triangle), NOS (dots),
and Seattle Marine Labs (hexagon).
-------
I
u>
t->
122* aor
f • 20cm I
122* 90r
C. 20- 25 m depths
Figure Vlll-1, Page 2
122* 30*
l" ¦ 20cm »"•
2
122* 30'
D. 35.9 - 98 m depths
-------
Strait; the other major stream continues toward the southeast
toward the entrance to Bellingham and Samish Bays. The
latter stream eventually re-enters Rosario Strait through the
various island passages. These include the net ebb flows in
Guemes and Bellingham channels.
In Bellingham Bay the net flows are variable in direction.
The Bay has a width that is comparable to its length. As a
result there is considerable lateral variation to the net
flows. The horizontal pattern may be inferred from plan views
of selected water properties obtained in various months
(Figure VIII-2, Appendix B).
The plan view of surface salinity (Figure VIII-2a) shows low-
est values penetrating southward along the western side of the
Bay and higher values penetrating northward along the Bay's
east side. This pattern suggests that there are main currents
moving southward and northward on the Bay's west and east
sides, respectively. As a result, effluent from the Nooksack
River and the GP mill tends to be carried southward out of
the Bay on the west side. Replacing this flow is Rosario
surface water entering on the east side.
The foregoing flow pattern also conforms to the effect produced
by the earth's rotation. That effect tends to direct the flow
to the right, where the observer is looking downstream. This
outflowing Nooksack River water tends to be driven to the west,
and inflowing water is driven to the east. Similar patterns
have been observed in other estuaries such asDabob Bay.
A portion of the surface current pattern in the Bay is shown
by the currents observed at approximately 3 m depth by
Collias (1971) . on the west side there sire southerly components
at all locations. However on the east side northerly flow is
not consistently shown by the measurements. There are several
explanations:
-312-
-------
A. SURFACE SALINITY
B. SURFACE SWL
Figure VIII-2 AVERAGE SALINITY AND SWL CONCENTRATIONS IN BELLINGHAM,BAY
Source: Collias and Barnes 1962
-------
• The current meters were moored from a surface
float so that surface waves may have contami-
nated the records;
• The observation depth of 3 m may be below the
seaward flowing surface layer;
• The records are relatively short ("20 days); and
• There are significant mean currents having time
scales on the order of several days that are
probably associated with winds (Figure VIII-3).
With respect to the second point, vertical profiles of salinity
often show freshwater concentrated in the upper part of the
water column. Examples of such salinity - depth relations,
as well as depth profiles of temperature, sigma-t, and oxygen,
are shown in Figures 111-12 & 13). With respect to the last two
points, Cannon (1973) has shown, based on measurements in
Puget Sound's Marine Basin, that record lengths of several
months are required to resolve current speeds of magnitude
2-3 cm/s.
The foregoing mean pattern is not in agreement with the flood
tide pattern reported by Collias et al. (1966). They inferred
a pattern based on movements of drifting objects during selected
flood tides (Figure Vlll-4). This pattern consists of flood
currents on the Bay's west side and concurrent ebb currents on
the east side. This pattern suggests that there may be a net
flood current on the west side and a net ebb on the east side.
The pattern of mean currents is in agreement with a composite
of patterns from Tollefson (1969), O'Keefe (1960), and Murty
(1960) as summarized by Sternberg (1961, Figure VIII-5) .
The water flowing southward out of the Bay tends to exit througn
the channel between Vendovi and Samish Islands. This is indi-
cated by the mean patterns of surface salinity and SSL. Both
patterns show a tongue that protrudes southward through this
-314-
-------
M
m
s
o
£
M
*
e
6
N T
d
at
*
o
u
*
O
*1
M 0
Figure VIII-3a. PERCENTAGE OF THE TIME THE WIND BLOWS FROM INDIVI-
DUAL (a) AND GROUPED (b) DIRECTIONS (16 DIRECTIONS
TOTAL) DURING EACH MONTH; AND WIND SPEED BY
DIRECTION (C) AND HOUR OF DAY (d) DURING EACH
MONTH. Source: Environmental Data Service 1975,
Pacific Northwest River Basins Commission 1969.
-315-
-------
c
1
1
I
'
k
i
1
•
i
1
<0 ^«)^»'*.!" " '» »' ¦ l^j'tn*"" " ^|>» *
XX-
g o.
Wy
Figure VIII-3b.
HOURLY VECTORS FROM 17 APRIL TO 7 MAY 1963
OF RAW CURRENT SPEED AND DIRECTION IN BELLINGHAM
BAY AND WIND SPEED AND DIRECTION RECORDED AT
THE BELLINGHAM AIRPORT.
Current meter moorings are shown in Figure VIII-1
and listed in Appendix A. Also shown are
Nooksack River runoff ana predicted tides for
Bellingham, Washington.
Source: Collias 1971
-316-
-------
K
Dt*TH (»)
i-C^Mu.
1 ¦ itiL f ijiil, , . 'Win* "j" i ' ' ^ i, ¦'« ~^>i'
«o ¦¦ 'i ¦ "»/r'»>>Vy5r'»W>^»'<'
^w/yr^ ^ ^V'
\ \' /V
\ V
W-'
t • t e it 1 4 U'm
TB—E—H ' W m—S—5—9—3"
MAY 196 S
Figure VIII-3c.
HOURLY VECTORS FROM 7-28 MAY 1963 OF RAW
CURRENT SPEED AMD DIRECTION IN BELLINGHAM
BAY AND WIND SPEED RECORDED AT THE BELLINGHAM
AIRPORT.
Current meter moorings are shown in Figure VIII-1.
and listed in Appendix A . Also shown are
Nooksack River runoff and predicted tides for
Bellingham, Washington.
Source: Collias 1971
- 317-
-------
*
|g o
'tmYfvww^v-v".
APRIL
ItftS
2
S
I
1 —
ao - -
r
M M fa
V
V
?#A
Figure VIII-3d.
HAY 1963
TIDALLY SMOOTHED CURRENT"METER RECORDS WITHIN
BELLINGHAM BAY VERSUS RUNOFF AND WIND CONDITIONS
Current meter moorings shown in Figure VIli-1.
Stick diagrams show net movement of water and
wind at hourly intervals.
Source: Collias 1971
-318=-
-------
LUMMI .
lbellingham
PULP MILL
PENINSUL
-t
POST POINT
ISLAND
GOVERNORS
:• POINT
SAAf/SH
BAY
GUEMES
I ISLANO .
Figure VIII-4 FLOOD TIDE CURRENTS IN BELLINGHAM
BAY
Source: Collias et al. 1966
-319-
-------
Y24q1 . —
lummi
BELLINGHAM
PULP MILL
ENINSULA
Murty
(1960)
POINT
1SLANO
GOVERNORS
POINT
Tollefson (.1959) W
& i
O'Keefe (1960)
SAMISH
GUEMES:
ISLAND '7^3*S
i z&n : iJ
Figure VIII-5 COMPOSITE PATTERN OF MEAN CURRENTS
Source: See text
-320-
-------
channel. Although the Bay water cannot be traced further
because of vigorous tidal mixing, the pattern of net currents
suggests that the effluent enters Rosario Strait through Guemes
and Bellingham Channels and then enters the Strait of Juan de
Fuca.
Some confirmation of the flow at surface has been shown by the
dispersion of oil spilled at the Texaco Refinery pier at Anacor-
tes during April 1971. Approximately 230,000 gallons were spilled
into Padilla Bay on April 26. Subsequently the oil drifted west-
ward through Guemes Channel, northward as far as Vendovi Island
and then southward via Rosario Strait into the inner Strait
of Juan de Fuca to Smith Island, and then westward (Figure VIII-
6). The dispersion pattern in Rosario Strait and Guemes Channel
appears consistent with net patterns of current obtained near
the surface (see Figure VIII-1). The northward flow may be
associated with tidal currents or winds that occurred at the
time of the spill.
2. Stratification and Vertical Mixing
It is useful to compare Bellingham Bay with characteristics of
other estuaries. Hansen and Rattray (1966) have introduced a
classification system that appears useful for the present
set of observations. In their method two dimensionless para-
meters are used: a stratification parameter, <5S/So (ratio of
surface-to-bottom difference in salinity, <$S, to the mean cross-
sectional salinity, Sq), and a circulation parameter, Ug/Uf
(the ratio of the net surface current, Us , to the mean cross-
sectional velocity Uf , Figure VIII-7).
This circulation parameter expresses the ratio between a measure
of the mean freshwater flow plus the flow of water mixed into
it by entrainment of eddy diffusion* to the river flow. The para
meter v represents the diffusive fraction (nongravitational
fraction) of the total upstream salt flux due to river flow and
-321-
-------
ORCAS IS
ttCLr
L0Pf2
BELLiNGHAM
LUttHU
,£UI» It-
MlSkSSJ?^4/26t l800
*C«OOvi H
4/27, 1330
IwX.,.
:7
*n%, orjo-s^p
f A *">--^3!
• ** s* «^*Tc
'^CJ
-;3 \Q
V?
-VI
MOfclA 1
jy-N
InuCkUBCMt it.
,f rUCAISK *
4/27,
800
noAtao
Figure VIII-6 TEXACO PIER OIL SPILL DISPERSION PATTERN,
APRIL 26/ 1971
Source: Vagners & Mar 1972.
-322-
-------
3b
Figure VIII-7. ESTUARINE CLASSIFICATION DIAGRAM OF HANSEN AND
RATTRAY (1966) AS ADAPTED BY CONOMOS (1979).
Parameters used are described in text.
Shaded areas are boundaries between estuarine typ$s$
Type 1: the net flow is seaward at all depths
and upstream salt transport is by
diffusion.
Type 2: the flow reverses at depth and both
advection and diffusion contribute
to upstream salt flux
Type 3s the salt transfer is primarly advective
Type 4: has intensive stratification with a
definite salt wedge.
Also shown are sub-classifications of weakly (a)
and strongly stratified estuaries (b).
Notation:
M Mississippi River mouth
C Columbia River Estuary
J James River Estuary
JF Strait of Juan de Fuca
NM Narrows of Mersey Estuary
S Silver Bay
AI Admiralty Inlet
PSMB Puget Sound's Main Basin
WB Whidbey Basin
NFSB Northern San Francisco Bay
BB Bellingham Bay
Sources: Hansen and Rattray 1966, Barnes and
Ebbesmeyer 1978, Conomos 1979.
Subscripts:
h high runoff
1 low runoff
w winter
s summer
Numbers to distance (in miles) from mouth of the
James River. -323-
-------
1 - v is that fraction accounted for explicitly by the gravita-
tional circulation. That is, when v = 1, gravitational circu-
lation ceases and landward salt transport is entirely by dif-
fusion (mixing}; as v approaches zero, diffusion becomes less
important and the upstream salt flux is almost entirely
accomplished by advection (from Conomos 1979).
During April and May 1963 there were measurements of water mass
and velocity sufficient to classify the Bay's western side. In
this computation the following data were used. The Us was
calculated as the mean speed at 3 n depth from sites A, B, and
J. The mean value was 3.8 cm s"1 based on 200 days of observa-
tion. The Uf was taken as the mean discharge of the Nooksack
River during April and May, 1963, divided by half of the cross-
sectional area of the Bay. The S/Sq was computed from oceano-
graphic observations made in May 1963 by Callaway et al_. (1963)
Figure VIII-7 shows Bellingham Bay parameters with respect
to other estuarine systems. In type 2 estuaries the flow
reverses at depth and both advection and diffusion contribute
to the upstream salt flux; in type 3 the salt transfer is
primarily advective. Thus it appears that in Bellingham Bay
the estuarine circulation is primarily advective.
It should be noted that the Hansen-Rattray diagram for estuarine
classification does not explicitly account for effects of winds.
In Bellingham Bay the winds are primarily directed from the south
in all months. This would tend to lower the value of Us • The
Us is further lowered because the current meters were moored
at 3 m depth rather than nearer the surface. We speculate that
longer records nearer the surface in the absence of winds would
give a classification farther to the right resembling a system
such as Whidbey Basin.
-324-
-------
3. Fluctuating Currents
The measured variance (variance as computed relative to the me am
velocity) in the current meter records provides an.indication
of the kinetic energy (KE) that might be available for the
mixing of effluent with marine water. The contribution of
tides to total variance (i.e., KE) can be computed as KE =
(TA-1 At"1 )2 , where A is a cross-channel section, T is the
change in water volume associated with the diurnal tidal range
landward of the cross-channel section, and t is a quarter tidal
day. The KE associated with tides has been computed from the
ocean entrance of the Strait of Juan de Fuca through Puget
Sound's Main Basin by Ebbesmeyer and Barnes (1980), and through
the Strait of Georgia in this paper; both are shown in Figure
VIII-8. The pattern consists of lowest values in Bellingham
Bay and an order of magnitude larger values in Rosario Strait
due to the tidal prism in the Strait of Georgia that must be
satisfied by water flowing through Rosario and Haro Straits.
A comparison of computed tidal KE and measured variance from
current meter records for selected cross sections of Puget
Sound, the Strait of Juan de Fuca, Haro and Rosario Straits,
and Port Angeles, Port Townsend Bay, and Bellingham Bay are
shown in Figure VIII-9 . The computed tidal KE corresponding
to cross sections in the Strait of Juan de Fuca and Puget
Sound are from Ebbesmeyer and Barnes QL980). The tidal KE was
computed for the San Juan Archipelago by assuming that the
tidal prism for the Strait of Georgia is satisfied simultan-
eously by water flowing through Haro, Rosario Straits, and
Middle Channel. This computed tidal KE is .44 m2s~2 based on
data of Waldichuk (1957, p 336). The computed KE for cross
sections in the study area are listed in Table III-2. The
measured variances from current meter records are those from
currents observed in The Narrows and Admirality Inlet by
Cannon et al. (1979), Pugrt Sound's Main Basin by Cannon and
Laird (1972), Port Angeles by Ebbesmeyer et al. (1979),
- 325-
-------
OCEAN
ENTRANCE DISTANCE MIANO (km)
e no too mo 400
I
ssz
LSI
E0>
M
X
&
* 9
Ife
m o
ieo-i
|to
I60
?so
"1 alTIMl KMC TIC
-t
M MISHWATf*
NCM BOTTOM
" V-'.'.u
«
*
¦
"1 ClOXVGCN NC*« ,r.
•
BOTTOM /yj —
/i i n
J
¦
tl
J
,i
' mi
4
©
0-2
m
m
u
"I
m |
u"
Figure VIII-8a. PROFILE DISTRIBUTIONS AT MID-CHANNEL FROM THE
PACIFIC OCEAN TO THE HEAD OF PUGET SOUND OF:
a) Tidal Kinetic Energy, b) Near Bottom Fresh-
water Percentage and Salinity, and c) Near
Bottom Oxygen Saturation and Concentration.
Source: Ebbesmeyer and Barnes 1980.
CURRENT METER SITES
.10
1620 W3
GUEMES
Channel
M
'l
M
E
ROSARIO
STRAIT
BELUN8HAM BAY
200
210
190
180
160
170
DISTANCE INLAND (km)
Figure VIII-8b. PROFILE DISTRIBUTIONS OF THE MEASURED VARIANCE
OF CURRENT METER RECORDS TAKEN AT MID-CHANNEL
IN ROSARIO STRAIT, BELLINGHAM AND GUEMES CHANNELS,
AND INTO BELLINGHAM AND PADILLA BAYS.
-326-
-------
M
(A
UJ
u
z
<
S
<
>¦
a
UJ
x
=5
<
UJ
2
01
0° -
0-1-
0-2-
0-3-
io-4
¦ r *
Ls.Wv<
AI/
•TN
.BB
PAH ~
/
SILL
ZONES
RS „
/'
/
¦>'K
' PUGET SOUND
MAIN BASIN
-CZ
-ITT
10-4 |0-3 10-2 10-1 100 101
COMPUTED KINETIC ENERGY (m*s-*)
Figure VIII-9 KINETIC ENERGY COMPUTED FROM TIDES VERSUS VARIANCE
FROM CURRENT METER MEASUREMENTS
Key:
BB - Bellingham Bay
RS - Rosario Strait
PAH - Port Angeles Harbor mouth
PT - Port Townsend bay
GV - Green Point - Victoria sill
AI - Admiralty Inlet
TN - Tacoraa Narrows
Sources: See Appendix A and Ebbesmeyer et al. 1979,
Cox et al. 1979, Cannon et al.~r97¥, and
Cannon and Laird 1972.
-327
-------
Port Townsend by Ebbesmeyer et al. (1979b), and the present
study area as listed in Appendix A.
At most locations tidal KE appears to be equivalent to measured
variance indicating that tidal processes are the major contri-
butors to variance. In Bellingham Bay# as with Port Angeles
Harbor and Port Townsend Bay, this is not the case. In Belling-
ham Bay at 3 m depth, currents typically reach speeds of .1 - .4
m s_1 and have a variance of .02 - .1 m2s~2(Appendix A), At.20 m
depth at stations G, H, and I current speeds typically reach
0.1 m s-1and have a mean variance of .015 m2s~2« Though these
variance are much smaller I.02/.51) than those measured in
Rosario Strait, they are substantially higher (.015 - .02/.0019)
than the tidal KE computed for the cross section at stations
G, H and I, indicating other factors contributing to the vari-
ance within the Bay. The anomalous energetics of Bellingham
Bay may be due to tidal eddies and local winds.
4. Water Properties and Related Wind Effects
In the surface waters of Bellingham Bay, physical variables
tend to follow the cycles of the local inputs (Appendix D). Thus
the surface salinity is inversely related to local river dis-
charge; surface temperatures follow the cycle of air temperature;
and dissolved oxygen in spring and summer is influenced by the
cycle of local primary production. WDF (Westley I960, Westley
and Tarr 1959, 1960) and Collias and Barnes (1962) data show
for SSL quite different seasonal cycles. The values of the WDF
are generally on the order of a magnitude in value larger than
those of Collias and Barnes, which may be due in part to differ-
ent observation periods. WDF records indicate maximum SSL
concentrations in March and September, times ->f lowest discharge
from the Nooksack aiver, and lowest values of SSL in January
and April - May, periods of highest Nooksack River discharge.
-328-
-------
In contrast, the data of Collias and Barnes (1962) do not show
a significant seasonal variation.
We have prepared patterns of winds which may be compared to
patterns of surface temperature, salinity, and SSL. Inspection
of these figures show that the patterns may be grouped into
categories:
• N-NE winds
• S-W-NW winds
• Southerly winds.
It is useful to discuss typical patterns for each category.
N-NE Winds: There were four surveys taken, all during autumn
(September - December) which showed winds prevailing from the
north. These patterns are generally consistent and show that
the freshwater concentrated near the surface and the SSL are
transported toward the shores of Lummi Peninsula and Island,
then southward along shore towards Vendovi Island. The most
prominent pattern occurred on 3 - 4 November 1960 (Figure
VIII-10). Under these winds the patterns show effluent from
the pulp mill can reach southward into Samish Bay. There are
also indications that on survey 2-4 November 1959 the efflu-
ent may be evident as far south as Puget Sound.
SW-W-NW Winds: Three patterns were obtained during westerly
conditions in Bellingham Bay during spring and summer 1960
(April, June, July). The most prominent pattern is shown for
21 - 22 June 1960 (Figure VIII-11). The westerly winds appear
to transport surface freshwater and SSL towards the east, with
some escaping Bellingham Bay to the south along shore past
Post Point. It is noteworthy that SSL is found in Samish
Bay (19 - 21 April 1960) when southerly winds prevailed in
Samish Bay and westerly winds prevailed in Bellingham Bay.
-329
-------
a) TEMPERATURE
W SALINITY
e) SWL
d) WINDS
Figure VIII-10 SURFACE DISTRIBUTION OF TEMPERATURE, SALINITY,
SWL AND WINDS FOR 3-4 November 1960.
Source: Collias et al. 1966 and Collias and
Barnes l5tT2
-330-
-------
o) TEMPERATURE
b> SALINITY
57!
17
'<
c) SWL
d) WINDS
1-
«••/ / _ *
¦r-v
JUNE 21, I960
1200
JUNE 22, I960
2400
Figure VIII-11 SURFACE DISTRIBUTION OF TEMPERATURE, SALINITY,
SWL AND WINDS FOR 21-22 June 1960.
Source: Collias et al. 1966 and Collias and
Barnes l5o"2
-331-
-------
Southerly Winds: Surface patterns were observed under prevail-
ing southerly winds during May and August I960, and February
1961 {Figure VIII-12). Under southerly winds, surface fresh-
water and SSL tend to be retained in Bellingham Bay; these
patterns show concentration changes primarily along the N-S
access of Bellingham Bay. The patterns also show relatively
uniform distributions east to west across the Bay except directly
adjacent to the mill (see Figure viii-12).
5. Residence Time
The bulk residence time may be estimated using three parameters:
freshwater, tidal prism and spent sulfite liquor.
Freshwater: The bulk residence time of freshwater in Bellingham"
Bay may be computed as the ratio of the total volume of fresh-
water contained within the Bay to the "volume to river flow (R)
per day. Collias et al. (1966) have estimated discharges of
the Nooksack River and Fishtrap Creek averaged for the seven
days preceeding each of their surveys. They obtained esti-
mates for 13 surveys which ranged between 1 to 10.7 days
(mean = 4.0 days with a standard deviation of 2.5 days).
Their calculations apply to an area north of Francis Island near
Post Point,
Tidal Prism: A useful measure of circulation is the ratio of
volume of water in the Bay to the volume of water between
MLLW and MHHW (i.e., tidal prism). The result is 4.7 tidal
prisms necessary for a complete change of water, assuming
total replacement of old water by new during each tidal
cycle. This result corresponds to approximately 2.5 days
during spring tides when two major changes of tide occur per
day.
-332-
-------
0) TEMPERATURE
b) SAUWTY
C) SWL
d) WINDS
AUG. 23, I960
AUG. 24, I960
Figure VIII-12 SURFACE DISTRIBUTION OF TEMPERATURE, SALINITY,
SWL AND WINDS FOR 23 - 24 August 1960.
Source: Collias et al. 1966 and Collias and
Barnes 1^72
-333-
-------
SSL: The bulk residence time may also be estimated for a
period when GP was closed by a labor strike. During the
period 12 ¦? 25 November there, were insignificant amounts of
SSL discharged. Observations of surface SSL were made on
18 and 25 November, and 1 December 1964. After six days of
closure (18 November ) SSL concentrations were considerably
reduced through the Bay, and after 13 days most SSL had been
removed from the the Bay, except for small concentrations in
the vicinity of GP (Whatcom Waterway). Background concen-
trations of 2-5 ppm were still evident; however, these were
not considered to be associated with the mill, as like values
can be found in the river and creeks discharging into RA. It
is estimated that 50% of the SSL was removed from the Bay with-
in four days (Figure VIII-13, VIII-14).
These observations occurred during a period when runoff of the
Nooksack was generally near its peak due to precipitation. The
runoff during June, November, December, January and February
from the Nooksack River was comparable. Collias et al. (1966)
estimated the bulk residence time from runoff from obser-
vations obtained during June, November, December, 1960, and
February 1961. The mean value was 2.2 days.
In contrast, during the mill closure six days were required
for SSL concentrations to drop by 50%. During November 1964
the Nooksack runoff was 80% of normal (10 year average from
1961 - 1970). We conclude that the residence time of SSL in
the system is somewhat longer than that estimated using tidal
prism and runoff. It may have been that the winds were
primarily southerly during this time, which would tend to
retain SSL in the system. Mora over it may be that an esti-
mate of six days is within the natural variability of the
system, since six days is within the mean plus one standard
deviation of Collias et al. (1966) bulk residence times.
In summary, considering the three approaches, the bulk residence
-334
-------
£
aMto»Mqt
TOO
*
4
SWL I
10 to <215
$
4
4
Samisn
Figure VTII-13 PATTERNS OF SURFACE SWL: a) Average for Nov.
1959-Nov. 1961, b) November 18, 1964, c) November 25, 1964,
and d) Deceiaber 1, 1964.
Source: USDI 1967
-335-
-------
80
70 -
60
50-
E
a
a>
40"
*
CO
30 -
33 V.
20-
MOX RESUMES
OPERATION
26 NOVEMBER, 1964
6.1? MILL SHUTDOWN
12 NOVEMBER, 1964
10-
IS
12
25
NOVEMBER (964 DECEMBER
Figure VXII-14 APPROXIMATE SWL CONCENTRATION NEAR MID-BELLINGHAM
BAY BEFORE, DURING AND AFTER A GEORGIA-PACIFIC
LABOR STRIKE. Data from Figure VI11-13.
- 336-
-------
time of Bellingham Bay appears to be on the order of a week.
Large variability can be expected due to influences of winds,
point of discharge, and amount of material input. There may
be differences in residence times due to the differences in
locations of the GP outfalls and the Nooksack River mouth.
6. Effluent Dilution Limits
The ratio of effluent discharge to the transport that occurs
naturally in the receiving waters may be considered an approxi-
mate limit to dilution assuming that complete mixing occurs.
A dilution limit is difficult to assess for the GP mill since
no current measurements have been taken near the outfall
locations prior to secondary treatment, and there is a lack
of flow data after the installation of the secondary treatment
diffuser. However, for the SP mill a volume transport of
2000 m3s~1is estimated to flow past Scott Paper's diffuser
located in Guemes Channel (after 1964). This value was
obtained by multiplying the average net current of 18.7 cm s"1
at site 23 by the cross-sectional area of Guemes Channel at
the site. The flow through Guemes Channel is assumed to be
sufficiently uniform that this volume transport applies to
the location of the SP diffuser. If the effluent were
completely mixed with this transport, the limiting dilution
would be 6897:1.
A more accurate description of the actual effluent dilution
taking place in RA can be achieved by observing the decrease
of various types of effluent tracers; in the case of GP and
SP mills, both are sulfite pulp mills and therefore SSL (PBI)
measurements indicate the actual distribution and concentration
of the effluents. As discussed before, the majority of the
SSL is found in the upper 3 m of the water column, with
highest concentrations at the surface. Therefore, it is of
limited value in describing horizontal dilution of the
effluent in both near, intermediate, and far distances from
the point of its discharge.
-337-
-------
Near Field Dilution: Approximate SSL concentrations within
the various outfalls of GP prior to dischar9e to marine waters
have beein estimated from surveys conducted in 1963 - 1964.
The data was presented in three reports .and is summarized by
the Washington State Water Pollution Control Commission (WPCC
1967; p. 33). Similar surveys were conducted for the SP mill,
the data being summarized by the same agency (WPCC 1967; p.
2X8).; however, the original reports were not obtained.
Additional information was provided by Bruce Johnson of the
Washington State Department of Ecology (personal communication).
For GP, average in-pipe SSL concentrations ranged from 773 ppm
(outfall #1) to approximately 350,000 ppm (outfall #3) during
the period of these surveys (see Figure 1-2 for outfall loca-
tions) . An average SSL concentration over 18 months of 2900
ppm has been reported within 200 m of the outfalls (WDF Station
No. 3A; Figure VIII-15). Assuming the SSL concentration from
outfall 3 to be the major source, the ratio of these values
gives a dilution of 121:1, or at station 3A, 0.83% of the ori-
ginal concentration. This value appears consistent with other
near field dilutions observed previously at West Point
(Ebbesmeyer and Helseth 1975), Port Angeles (Ebbesmeyer et al.
1979 ), and Port Townseiid (Cox et al. 1979).
For the SP mill, in-pipe SSL concentrations average approxi-
mately 73,400 ppm. An average concentration of 285 ppm has
been reported within 200 m of the outfall (WDF 17) giving a
dilution of 258:1, or at Station 27 0.39% of the initial
concentration, or a decrease of 336 ppm per meter assuming a
linear decrease (See Figure VIII-16 for outfall locations).
Intermediate and Far Field Dilution: To estimate dilution
rates beyond several hundred meters of the outfall, average
SSL concentration at stations taken regularly by the WDF from
-338-
-------
Strait of
Georgia
Lummi Bay
Lomntt
Gooseberry
Pt.
BeJWnghanrt
Portaga
HI.
Portag*
Pt. Frances
Chuekanut Bay
Pleasant Bay
inati Bay
Eliza laL
uMiintf
\ V »•»;
Wildcat Cova
Sinclair
Isl
San Juan
Islands
Sami«h Bay
Fiah Pt.
ftnaeortea
Padllla Bay
100 200
150 300
thousands of foot
'Figure VIII-15 SELECTED WATER QUALITY STATIONS SAMPLED BY THE
WASHINGTON DEPARTMENT OP FISHERIES September 1956-
November 1957
Source; Westley 1957, Westley and Tarr 1959, Westley 1960
-339-
-------
I
OJ
0
1
Nautical Miles
mums
mBm
• Scott Paper Company
pulp mill
City of Anacortes
sewage treatment plant
Sebastian Stuart Fish
Co. cannery
Fishermen's Packing
Corp. cannery
Shell Oil Company
oil refinery
Texaco Inc. oil
refinery
Point of waste
discharge
Ch«nn«/
Pa d i II a
Bay
ftftjfltiorfM
ISLAND
F1DA LG0
Figure VIII-16
WASTE SOURCES IN THE ANACORTES AREA (1964)
Source: USDI 1967
-------
1957 -.1959, Collias and Bairnes from 1959 - 1961, and Cardwell
from 1961 - 1976 were plotted versus the distance of the station
along a central axis running from the Gi> outfalls in Whatcom
Waterway to the SP outfall in Guemes Channel (Figure VIII-17) .
A station's distance from the end points is estimated by the
intersection of a line perpendicular to the center line and
which passes through the station's location. The SSL observa-
tions show a fair amount of scatter, though there are indications
of a possible exponential decrease beyond three kilometers.
SSL concentrations reach 10 ppm at approximately 15 - 20 km.
Corresponding additional dilution of the GP effluent at this
point is 290:1, or a total dilution of 35,000:1. The effluent
at this point is only .002% of its original concentration.
The SP effluent is diluted to similar levels much more rapidly,
and appears to add little to any background SSL concentration
in the RA system. Average SSL concentrations of 2 ppm were
reported by Cardwell and the WDF within 2.5 km of the outfall,
an additional dilution of 143:1, or a total dilution of approxi-
mately 37,000:1. Because 2 ppm of SSL is near or below the
accuracy of the SSL testing procedure for pulp mill effluent,
it is doubtful that the SP mill added any significant amount of
SSL on a long term basis to the average values found at hydro-
graphic stations within RA.
-341-
-------
outyicls
*ooo<
S-P OUTFALL
1000-
A a
• 100-
•J
*
>
S
t
IS
• *
B •
V
# • •
.•44 *
•.\r
a fb t»
OSHMCE PROM NOOKSACK RIVER MOUTH (ton)
Figure VIII-17.
SWL (top) AND SALINITY (bottom) VERSUS THE SHORTEST
DISTANCE BY WATER TO THE STATION PROM THE GEORGIA-
PACIFIC MILL AND THE NOOKSACK RIVER MOUTH, RESPECTIVELY.
Station sources: Collias and Barnes (1962,, dots),
WDF (squares), and Cardwell and Woelke (1979,
triangles).
-342-
-------
B. WATER QUALITY
It is clear from the preceding oceanographic analysis that
effluents emanating from the Georgia-Pacific Mill are likely
to encounter highly variable current patterns, depending mainly
on tides, winds and Nooksack River inflow at the time of emis-
sion. Water quality effects of these effluents can thus be
expected to exhibit a patchy, sporadic nature. This makes
analysis through correlation or other statistical means ex-
ceedingly difficult. In most cases, the environmental
influences are not completely known during water quality samp-
ling. periods. The fluctuation between conditions of violation
and non-violation of standards at a given station may therefore
be due to changes in currents, winds or other factors.
1. Water Quality Violations
Pre-primary treatment violations in the vicinity of Georgia-
Pacific have been well documented from measurements by WDF
(Westley i960), USDI (1967) and others. As summarized in
Chapter IV, SSL values during these periods were strongly tied
to low pH and DO, with DO values frequently dropping below
5 rag/1 in the inner harbor (Class B waters) and sometimes
dropping below 6 mg/1 in Class A waters.
Post-primary treatment data at Bellingham is considerably less
complete. STORET data exists for only a few stations, of which
only station BLL006 continues to operate in the Harbor, near the
mill (Figure VIII-18). This station has shown DO values less than
5 mg/1 on occasion (3.4 mg/1 minimum) . Of the STORET stations in
Class A waters, stations BLL009 and 010 have recorded readings
slightly above the standard of 6.0 mg/1 (6.2 mg/1 minimum for
BLL009, 6.5 mg/1 minimum for BLL010)? however, no violations of
Class A water standards have been recorded at these two stations.
CH2M Hill data for 1974 and 1975 show violations of both pH
-343-
-------
Strait of
Georgia
Portaga
*
BLLOIO®
San Juan
Islands
VIII-18 SELECTED WATER QUALITY STATIONS USED IN THIS
REPORT.
-344
-------
and DO in both surface and deeper (20 m) waters. Since these
data were taken near Post Point, some distance from the mill,
they have only inferred value for analyzing Georgia-Pacific
effluents. The readings may represent occasional migration of
the effluent down the east side of the Bay during particular
tidal conditions. Values below 6.0 do occur occasionally.
Webber (1978) presents the only data useful in assessing
general water quality near Georgia-Pacific Corporation after
primary treatment and before installation of secondary treat-
ment or the submarine diffuser. Webber's data show that DO
was extremely low in some cases, reaching 0.0 at times in
Whatcom Waterway. Other violations occurred near Squalicum
Creek. Table VIll-1 summarizes this data for major water quality
parameters, indicating violations of state standards as defined
by Table IV-1.
Although not always sampled, there have been other violations
of water quality standards associated with spills (see Table
1-7). During the period following installation of primary
treatment, Georgia-Pacific's Bellingham mill has averaged
11.5 spills or violations annually through 1978. Even after
installation of secondary treatment, leaks in the treatment
lagoon have caused numerous pollutant spills near Whatcom
Waterway (see Table 1-7). STORET data, however, shows no
oxygen violations since June 1979. While this may indicate
that secondary treatment has improved conditions in the
Bay in general, it cannot be taken to indicate that no more
violations occur, due to the small number of stations and
their locations relative to the new discharge point.
2. Treatment Processes and Deepwater Diffuser
Comparisons of water quality levels in the Bay before and after
installation of Georgia-Pacific's primary treatment process is
made difficult by the lack of uniform station locations in
-345-
-------
Table VIII-1
Source:
SEASONAL HATER QUALITY MEASUREMENTS AND VIOLATIONS IN INNER BELLINGHAM BAY 1977 - 1978.
Webber 1978
D.O
PH
Turbidity (NTU)*
Violations**
S
F
W
Sp
S
F
W
Sp
S
F
W
Sp
S
F W
Sp
Class A Stations
Mt. Baker Plywood
N/D
N/D
6.8
8.7
N/D
N/D
N/D
N/D
N/D
N/D
N/D
N/D
-
-
-
Squalicum Creek
Inner
9.2
9.6
8.8
9.8
7.3
7.8
7.6
7.3
6.0
5.0
3.0
2.3
_
— —
Mid
9.1
0.0
7.7
1.7
7.3
7.8
7.5
7.5
4.0
3.5
2.0
3.1
-
D
D
Outer
7.3
7.4
8.1
7.3
7.4
7.5
7.3
7.3
2.5
4.0
1.5
1.9
-
-
-
Open Water Disposal
N/D
N/D
N/D
9.3
N/D
N/D
N/D
7.7
N/D
N/D
N/D
0.5
-
-
-
Bay
8.9
9.9
9.4
N/D
7.9
8.1
7.4
N/D
4.5
0.7
1.5
N/D
-
¦-
-
Boulevard
9.0
6.9
N/D
N/D
7.9
7.5
N/D
N/D
1.0
1.0
N/D
N/D
- -
-
-
Class B Stations
I & J Waterway
Inner
7.7
1.9
7.5
5.2
7.1
6.6
5.9
6.7
5.2
2.5
1.8
2.6
—
D.P P
P
Mid
8.8
1.5
8.3
1.9
7.5
6.7
7.4
6.4
16.0
2.5
1.6
4.7
T
D.P
D.P
Outer
9.2
3.9
8.1
4.0
7.4
N/D
7.4
6.5
22.0
2.0
1.7
4.0
T
D
D.P
Whatcom Creek
Inner
1.2
3.0
2.4
3.2
2.9
4.4
6.0
5.6
16.0
10.0
o
•
o
6.0
D.P,
T D.P D.P
D,P
Mid
9.1
0.0
7.7
1.7
7.2
5.8
7.2
5.7
22.0
4.5
2.1
4.9
T
D,P
D.P
Outer
9.1
6.6
8.1
8.6
7.5
7.3
7.6
7.5
14.0
0.9
1.3
0.7
T
-
-
Old Disposal
7.6
6.1
9.1
N/D
7.5
7.3
7.7
N/D
1.5
1.0
2.0
N/D
-
-
-
I
u>
-------
each major study. The WDF data (Westley 1960) provides the
pre-primary, treatment data base, while Webber's 1978 data pro-
vides the most complete post-primary information, at least
for the harbor and parts of the Northern Bay.
Table VIII-2 shows selected monthly data during each season at
comparable sampling stations before and after installation of
primary treatment. Station 1 from WDF data is located close to
4 of Webber's stations (Mount Baker Plywood, Inner-, Mid- and
Outer-Squalicum stations; see Figure VIII-18)', and water
quality levels between these two groups should be roughly
comparable. Table VIII-2 shows average values (x) for each
month shown. The differences in surface DO readings between
pre- and post-primary data from these stations are 3.47 mg/1
in January, 0.77 mg/1 in April, 0.45 mg/1 in July and 2.48 mg/1
in October. In all cases, Webber's post-primary treatment data
shows lower values of surface DO. This may be due to increases
in mill production between the late 1950's and late 1970's
(which can be expected to cause DO depletion) coupled with
the BOD reductions caused by primary treatment (which can be
expected to enhance DO values). In any case, it is clear
that DO depression has not been completely reduced by primary
treatment and that severe DO violations still exist at some
stations.
The second data set shows Stations 3 and 3A, which are close
in location to six stations near the I and J and Whatcom
Waterways. These data indicate that DO levels are improved
during the spring, summer and fall periods; however, winter
values were lower. The respective increases (+) and decreases
(-) were: January, -1.97, April +1.18, July +3.61, October
+1.47. This indicates a general DO improvement in the inner
harbor of 1 to 3 mg/1 with primary treatment. It is also
clear that serious violations did still occur after primary
treatment, both in the I and J area and Whatcom Waterway.
Secondary treatmeint can be expected to improve this situation
-347-
-------
Table VIII-2. SURFACE DO LEVELS (mg/1) AT COMPARABLE STATIONS
BEFORE AND AFTER INSTALLATION OF PRIMARY TREATIiENT
Station
Year
January
April
July
October
1
1956
—
—
—
9.87
1
1957
—
—
—
6.81
1
1958
11.12
7.65
3.93
7.78
1
1959
11.53
— .
—
X
11.32
7.65
9.98
8.15
3
1956
__
_ _
2. 83
3
1957
—
—
1.14
3
1958
11.50
3.81
9.24
. 36
3
1959
8.26
3.22
3.11
—
3a
1956
—
—
—
2.99
3a
1957
--
—
—
.26
3a
1958
8.06
4.68
3.3
0.0
3a
1959
8.14
0.0
0.0
—
X
8.99
2.92
3.91
1.35
Source: Westley
1957#
Westley &
Tarr 1959,
Westley &
Tarr 1960
Mt Baker Plywood
1977-8
* 6.8
8.7
--
—
Inner Squalicum
M
8.8
9.8
9.2
9.6
Mid Squalicum
It
7.7
1.7
9.1
0.0
Outer Squalicum
tv
8.1
7.3
7.3
7.4
(Compare with No. 1, above) x
7.85
7.88
8.53
5.67
I & J Inner
1977-8
* 7.5
5.2
7.7
1.9
I & J Mid
•t
8.3
1.9
8.8
1.5
I & J Outer
t«
8.1
4.0
9.2
3.9
Whatcom Inner
H
2.4
3.2
1.2
3.0
Whatcom Mid
II
7.7
1-7
9.1
0.0
Whatcom Outer
It
8.1
8.6
9.1
6.6
(Compare with 3 & 3a, above) x
7.02
4.10
7.52
2.82
Source: Webber 1978
* July and October 1977; January and April 1978
-348-
-------
both through aeration and bacterial action; however, a suffi-
cient data base is not yet available to make an actual assess-
ment.
Data from station BLL006 (the only operating STORET station
near Georgia-Pacific) does show an increasing trend in surface
DO levels (Figure-VIII-19)f as do stations BLL008, 009 and 010,
indicating some overall improvements in Bellingham Bay water
quality during the 1970's. This is probably due in part to
primary treatment. By-product recovery improvements and
SSL reductions during the 1970's may also have played an
important part.
The sharp depression of. DO values during late-summer 1979,
after installation of secondary treatment is probably due to
two factors. The decline corresponds to mid-year decreases
which have occurred in many of the previous years (see Figure
VIII-19a and b) corresponding to a lower freshwater inflow rate
and late summer increases 'in stratification. It may also be due
to the fact that numerous leaks occurred in the secondary treatment
lagoon during this period. The accumulation of longer term post-
secondary treatment data should eventually clarify this trend.
In conjunction with the installation of secondary treatment,
Georgia-Pacific installed a deepwater diffuser in 1979. The
purpose of the diffuser was to carry wastes away from the
shoreline environment, into waters where they would mix and
dilute more quickly. From available oceanographic and water
quality data, it is clear that the diffuser alone would bring
some improvement in inner harbor water quality levels. Dis-
charging into Class A waters, however, violations outside of
a dilution zone could still occur without secondary treatment.
Unfortunately, accurate comparisons of currents and dilutions
between the inner harbor and the diffuser location cannot be
made due to lack of data, in Chapter III, only gross current
directions were computed for these near-shore currents since
-349-
-------
Figure VIII-19a TIME HISTORY OF DISSOLVED OXYGMt*AT SELECTED STORET STATIONS
-------
I*4L
B11009
0LLO1O
»Q
Q
1 i M 4 1 N
J « H 4 S »
i at m i h m
r-i . i i M ¦ i ¦
4 M M 4 in
rr-r-rr i "
4 M tf 4 S M
r*r —i—i
J « « J t «
; :: j ;»
4 M M J i M
» m i» 4 i a
J i i J i i
r—i—i—i—i—r
4 m m i • m
T 1 1 1 1 • f
4 M M 4 • «
lift
fto
tin tin
lift
mi
Itfft
iirt
•n
ftrt
Figure VIII-19b TIME HISTORY OF DISSOLVED OXYGEN AT SELECTED STORET STATIONS
-------
velocity data was not available.
It is therefore somewhat uncertain as to whether the diffuser
alone, without secondary treatment could improve water quality
to meet basic State standards for DO. Turbidity and pH are
also uncertain to some extent, although for these parameters
it appears that only occasional violations have occurred
during the post-primary treatment period. Even with improve-
ments to standards, however, use of the deepwater diffuser
alone, without secondary treatment, would not reduce the over-
all toxic discharge into the Bay. There is considerable evi-
dence (see Chapters I, II and V) that secondary treatment does
reduce toxic discharge.
C. TOXICITY
In-plant effluent toxicity has been tested in only 3 bioassays
documented by Georgia-Pacific. In addition, a few studies have
been conducted by State and Federal agencies. These data are
briefly analyzed below in subsections 1 and 2. The bulk of
this section, however, is devoted to analysis of oyster larvae
bioassays which provided a long-term data base from a statis-
cally significant number of stations. This will be analyzed in
Subsection 3, below.
1. In-Plant Effluent Bioassays
The first -two bioassays recorded by known Georgia-Pacific cor-
respondence are comprised of both untreated and primary treated
effluent. It is clear from the data that primary treatment
significantly reduced the effluent toxicity. For treated
effluent, one test*shows an LC50 of 38%, while the other shows
83%. The large discrepancy in the two values may indicate a
352
-------
different method of analysis, large variation in mill effluent
toxicity over time, or improvements in effluent during the
three year period between bioassay dates. From the data, it
is impossible to determine which of these is the actual reason
for the discrepancy.
The data from the December 13, 1977 bioassay (see Table V- 3)
indicate an LC 50 of 83%. The data presented, however, only
record values at 65% and 100%, with none in between. It appears
that the 83% claimed is only an estimate based on a linear
approximation. The data do not show that toxicity to mill efflu-
ent is a linear function. Therefore, the 83% LC 50 may be
considerably in error. The 1974 bioassay does not show how
the LC50 was computed; however, since a similar technique was used,
this may also be in error.
3. Agency Fish Bioassay Studies
The majority of agency studies have focused on acute effects
of mill effluent to adult or juvenile fish. These studies were
conducted previous to primary treatment or SSL reduction by
the mill. In these conditions, SSL can be used as an effective
indicator of toxicity.
The fish bioassays clearly show a differentiation in response
by each species, even those in the same general group (i.e.
trout and salmon). Differences in excess of a factor of 3 are
found for salmon and trout species. It may therefore be pre-
sumed that marine fish in other groups have a susceptibility
variation at least this large, possibly greater.
Host fish tested did not show large lethal response until SSL
levels neared 500 ppm. Chronic or sublethal effects have not
been documented and may well occur at considerably lower SSL
levels. English sole eggs (USDI 1967) show a sharp mortality
-353-
-------
increase at about 180 ppm PBI for fry development. The
threshold value for this response seems to occur near 15 ppm
PBI (see Figure V-6).
Following primary treatment, no agency studies are available.
Although SSL levels dropped substantially following primary
treatment installation and during SSL reductions during the
1970's, it is not clear what lower SSL indicates in terms of
reduced toxicity. Much of the available literature indicates
that SSL is not the toxic component of mill effluent and may
not be tied closely to acute toxicity (Hutchins 1979).
3. Oyster-'Larvae Receiving Water Bioassays
Data from the WDF Compendium (Cardwell and Woelke 1979) were
analyzed with respect to both abnormality and mortality
effects. Analysis previously performed by WDF was not used
since Cardwell (personal communication) has indicated that those
data with salinities less than 20 ppt should be deleted. The
compendium data were also updated by more recent data from
WDF.
Table VIII-3 shows the mean percent abnormal statistic for the
period from 1961 - 1972 and 1973 - 1978 declined from 14.3 to
12.7 percent, along with a decline in the PBI concentration
from 30.3 to 24.9 ppm. A similar reduction in mean percent
abnormality was found by analyzing the data by depth for the
two time periods; however, little change in the mean PBI
concentration occurred. It is apparent that primary treatment
resulted in only limited reduction in the toxicity of the
receiving waters in northern Puget Sound. The average mortal-
ity percentages remained about the same for both periods at
20%.
-354-
-------
Table VIII-3i SUMMARY OF WDF COMPENDIUM DATA FOR YEARS AND
AND DEPTHS PRIOR TO AND FOLLOWING PRIMARY
EFFLUENT TREATMENT AT GEORGIA-PACIFIC MILL IN
BELLINGHAM*
Variable
Mean %
Abnormal
SD
PBI
SD
Salinity
SD
n
1961 -72
14.3
.3232
30.3
124.59
26.95
2.27
605
O
1
B
14.5
.3259
30.9
125.77
26.91
2.28
593
1973 - 78
12.7
.3149
24.9
105.08
27.83
2. 33
540
0 - 3 m
12.6
.3095
30.2
120.87
27.38
2.45
378
> 4 in
12.7
.3231
12.7
50.44
28.86
1.62
162
Variable
Mean %
Mortality
SD
PBI
SD
Salinity
SD
i l
n
1961 - 72
19.6
.2424
30. a
124.59
26.95
605
0-3 vsl
19.8
.2429
30.9
125.77
26.91
593
1973 - 78
20.8
.2978
24.9
105.08
27.83
593
0 - 3 m
21.1
.3023
30.2
120.87
27.38
378
> 4 in
20.3
.2876
12.7
50.44
28.86
162
* Data from 32 stations in Northern Puget Sound with salinities
>19.99 ppt. Source: Cardwell and Woelke 1979.
-355-
-------
The data were then analyzed by the 32 stations in northern Puget
Sound for the period 1961 - 1972 and 1973 - 1978. Responses
from depths ranging from the surface to 3 m at each station
were combined, as were those at depths greater than 4 m.
Only surface samples were collected from 1961 - 1970 and routine
subsurface samples began in 1973. The stations in Table V-1.0
were ordered by grouping in concentric circles at increasing
intervals from the source of the Georgia-Pacific mill effluent
(see Figure V-7). A direct relationship between mean percent
abnormal and mean PBI concentration was evident during both
periods before and after the initiation of primary treatment
in 1973. A similar relationship to PBI concentration and per-
cent abnormal response was reported by USOI (1967), although
the limitations of the PBI have been pointed out repeatedly
by Barnes et al. (1963) and Cardwell et al. (1976) . Graphic
representation of these data (Figure VIII-20)indicate primary
treatment generally reduced the extent of toxicological impact
of the pulpmill effluent; however, it remained high in the
vicinity of the mill and along the east shore of Bellingham
Bay. Although comparable samples were not taken during the
1961 - 1972 period from depths greater than 4 m, toxicity due
to SSL was apparent after primary treatment begem.
The toxicity maps presented for north Puget Sound by Cardwell
and WoeIke (1979) were adjusted to remove the influence of
freshwater. The salinity criterion of 20 ppt or greater was
utilized, as well as the greatest abnormality or mortality
response at any depth at each station for each year. Symbols
designated the abnormality and mortality responses at levels
of 5 - 19, 20 - 49 and > 50 percent by year. The resulting
toxicity maps are presented in Appendix F. in general,
receiving-water toxicity was found in the vicinity of the
pulpmill and along the east shore of Bellingham Bay; however,
the maps lack consistency due to the variable interference by
freshwater.
-356-
-------
ioo-
90—
-1961 1972
-1973-1978
<
2
oc
O
z
tn
<
»-
z
1*1 50-
O
AC
Ui
40-
z
<
UI
S
30-
20-
10-
S
Oi
•o
STATION
Figure VII1-20. COMPARISON OF MEAN PERCENT ABNORMAL RESPONSE OF OYSTER LARVAE AT
32 STATIONS.
-------
An analysis comparable to that conducted by Cardwell and Woelke
(1979) ajid Cardwell et al. (1979) for east and west central
Puget Sound was conducted on the receiving-water bioassay data
for Bellingham Bay (Cardwell and Woelke 1979). Two analytical
approaches were followed. The first tested for changes in the
biomonitoring responses (abnormality and/or mortality of
Pacific oyster larvae) to surface water samples over a series
of years from 1968 through 1977. This time period began
before and extended beyond the initiation of primary treat-
ment by Georgia-Pacific in 1973. A series of 11 stations at
successive distances from the outfall in Bellingham Bay
were utilized. In analyzing these data with multi-factorial
ANOV, the date and location of the sample were treated as
separate factors and salinity, PBI and seawater age as covari-
ates. The age of seawater from the time of collection to analysis
has been included in all similar analyses by Cardwell and Woelke
(1979) because it is an additional factor which could affect
the toxicity of the sample. The second approach tested five
seasonal samples taken during 1973 and 1974 at seven stations
and three depths. All samples were taken after initiation of
primary treatment of the pulpmill effluent and serve to demon-
strate the extent of the toxicity remaining in Bellingham Bay.
In analyzing these data with multi-factorial ANOV, the date,
location and depth of the sample were treated as separate
factors and salinity, PBI and seawater age as covariates.
The receiving-water data for surface-water samples taken at
eleven stations from 1968 to 1977 are summarized in Table
VIII-4 with associated salinity, PBI and age of seawater.
Visual inspection of the data revealed that receiving-water
effects on abnormality and mortality of larvae varied consid-
erably between stations and to a lesser extent between years.
The highest PBI concentrations generally occurred with salin-
ities less than 20 ppt which resulted in an additive effect
of both parameters on the larval responses. Even though this
interaction existed, the ANOV was conducted in an effort to
-358-
-------
Table VIII-4. HISTORICAL VARIATION IN QUALITY AND ACUTE TOXICITY TO
PACIFIC OYSTER LARVAE IN SURFACE RECEIVING WATERS
Date of Sampling
Station 7/22/68
7/8/69
7/20/70
7/12/71 6/14/72
6/19/73
8/06/74
8/12/75
8/31/76
7/11/77
Abnormal
Shell
Development of Larvae
(%)
01-1115
33. 33
100.0
99.45
100
100
100
100
100
100
100
01-1417
97.36
100
100
100
100
100
99.39
100
100
65.18
01-1620
100
100
100
100
100
100
0
100
100
3.83
01-2217
32.29
0
100
0.18
0.04
1.38
0.21
98.62
33.29
4 . 32
01-3013
12.65
0
0.61
6.30
0.52
0.03
0
0.04
0.21
0
01-3308
0
0
0
0.07
0
0.51
0
0.29
0
-
01-2731
0
2.77
0.09
0.56
92.80
100
0
0
0.66
0
01-1644
2.39
0
0.53
1.00
0
98.19
0
0.37
0.88
5.21
01-4115
0.15
0.51
0
0
22.6
0.22
0
2.26
0.38
1.23
01-3926
0
0. 30
0.05
10.22
0.17
0.72
0
0.06
0
0
01-3236
4.37
13.43
0.07
0.43
0.48
o: 03
0
0
0.57
5110
A
Mortality of Larvae (%)
01-1115
99.21
100
21.6
100
41.14
100
100
100
69.06
3.87
01-1417
79.21
99.83
65.99
100
100
87.31
100
41.52
17.10
61.6
01-1620
53.95
93.89
52.85
100
98.38 79.66
14.82
54.18
32.81
38.67
01-2217
42.63
6.15
14.69
4.10
8.86
0
10.35
68.12
27.49
64.09
01-3013
21.84
12.36
5.42
13.73
23.31
0
79.47
5.45
6.25
70.17
01-3308
21.14
14.47
8.33
13.55
40.32
0.12
96.75
6.26
9.26
-
01-2731
9.56
61.65
20.5
9.89
88.66
0
55.48
7.74
25.42
90.88
01-1644
17.72
61.82
9.30
8.20
0
24.53
28.04
19.98
8.10
81.49
01-4115
6.40
0
10.12
31.01
70.83
0
50.19
26.74
3.25
0
01-3926
8.25
30.25
11.23
26.93
3.36
0
70.73
8.16
0
4.42
01-3236
0
54.69
11.10
14.54
6.99
0
31.29
2.09
0
86.46
Salinity
(ppt)
01-1115
9.87
5.07
12.59
9.40
11.4
10.3
8.3
14.2
8.0
10.2
01-1417
17.36
11.96
23.55
10.23
1.2
22.10
15.9
13.3
12.3
27.3
01-1620
12.95
17.7
23.77
6.89
15.6
22.10
18.8
12.2
16.9
27.3
01-2217
25.53
26.91
25.01
22.54
21.8
30.0
19.9
25.1
25.0
29.8
01-3013
23.28
28.89
28.08
2.38
24.7
29.5
24.9
28.0
27.3
29.5
01-3308
25.17
28.86
27.79
25.79
24.0
29.6
25.7
29.0
26.3
-
01-2731
22.18
25.48
27.75
24.36
16.50
23.3
23.9
28.0
26.2
29.5
01-1644
21.37
25.86
27.97
22.83
25.7
18.3
23.0
27.3
26.1
29.5
Continued.
-359-
-------
Table Vili-4, page 2.
Oate of Sampling
Station 7/22/68.7/8/69 7/20/70 7/12/71 6/14/72 6/19/73 8/06/74 8/12/75 8/31/76 7/11/77
Salinity(ppt)(Continued)
01-4115
16.56
24.63
27.48
27.41
13.7
19.5
23.10
26.5
26.1
27.2
01-3926
24.65
27.12
29.07
26.08
27.9
28.9
24.2
28.5
27.9
29.8
01-3236
22.32
27.14
28.19
27.43
26.4
28.4
23.3
28.0
28.1
29.1
Pearl-Benson Index (ppm)
01-1115
460
3140
-
635
525
735
1560
2100
416
384
01-1417
291.5
176
108
115
0
760
81
322
226
26
01-1620
327.5
600
99
175
128
360
16
100
338
0
01-2217
29
21
47
17
26
3
18
43
48
19
01-3013
9
0.5
3
21
14
1
0
0
1
0
01-3308
7.5
0
3
2
14
2
0
0
3
. I
01-2731
2
6.5
9
13
73
59
7
5
4
I2
01-1644
1.5
22
8
19
4
52
0
9
1
'o
01-4115
4
2
0
1
0
1
0
15
4
0
01-3926
18
24
5
2
9
5
3
2
2
0
01-3236
1
0.5
6
5
-
9
0
3
1
5
Age of
Seawater
¦ (minutes)
01-1115
255
160
232
305
396
430
457
420
414
413
01-1417
250
165
230
303
394
418
445
410
420
400
01-1620
245
169
227
299
390
415
444
405
428
395
01-2217
242
173
224
297
388
410
434
395
431
389
01-3013
239
177
222
294
385
400
426
386
456
381
01-3308
235
182
218
291
382
350
399
361
459
-
01-2731
217
118
197
268
360
390
416
373
443
372
01-1644
265
123
242
346
405
455
478
443
399
432
01-4115
227
190
211
285
374
365
392
349
470
349
01-3926
223
194
207
281
371
375
385
343
474
342
01-3236
215
115
200
275
362
380
413
375
448
366
Source: Cardwell and WoeIke 1979.
-360-
-------
attempt to discriminate variation in toxicity between station
and years to determine if primary treatment had reduced toxicity
to the Bay. Larval abnormality was affected significantly
(p < 0.001) by both factors, the interaction between factors
and salinity. Age of seawater and PBI were not significant.
Of the total variation in larval abnormality 55% was explained
by sampling station, while the interaction between sampling
date and station accounted for an additional 17%. Salinity
accounted for 10% of the variation.
The results of the ANOV using larval mortality as the criterion
variable indicated that both salinity and PBI were significant
(p < 0.001), while seawater age was not (Table VIII-5). Sam-
pling location and date were almost equally important in ex-
plaining 26 and 24%, respectively, of the total variability.
Salinity remained the most important covariate, explaining 3%
of the total variation, while PBI explained 1.0% and the age
of seawater had no significant influence. Interaction between
date and station accounted for 29% of the variation.
When the data were ordered in terms of relative effects of
dates and stations on abnormality and mortality, the abnormal-
ity criterion indicated the years preceding 1973 were signif-
icantly more toxic than those following 1973 (Table VIII-6).
However, no discernable pattern between years was apparent
for the mortality criterion. Ranking of the stations indicated
those nearest the outfall were most toxic regardless of the
toxicity criterion? however, these stations were also most
affected by freshwater discharge into the Bay.
The receiving-water bioassay data from quarterly samples in
Bellingham Bay (Cardwell and Woelke 1979) from mid-1973 to
mid-1974 are summarized in Table VIII-7. The results of the
ANOV's with respect to abnormal development and mortality of
oyster larvae are presented in Table VIII-8 and VIII-9. Date,
station and depth and their interactions accounted for signif-
-361-
-------
Table VIII-:5. EFFECT OF VARIOUS FACTORS ON ABNORMAL SHELL DEVELOPMENT
AND MORTALITY OF PACIFIC OYSTER LARVAE IN BELLINGHAM
BAY SURFACE WATER SAMPLES (1968 - 1977).
Sum of Mean
Source of Variation Squares d. f. Square F Significance
ABNORMAL DEVELOPMENT
Factors
Sampling date
2,883
9
.320
3.832
.001
Sampling location
38.620
10
3.862 ¦
106.461
.001
Covariates
Salinity
7. 038"
1
7.038
193.996
.001
PBI
.038
1
.038
1.053
.306
Age of seawater
.033
1
.033
.907
.342
2-way Interactions
12.150
89
.137
3.763
.001
Residual
10.121
279
.036
TOTAL
70.097
390
.180
MORTALITY
Factors
Sampling date
11.582
9
1.287
45.150
.001
Sailing location
12.633
10
1.263
44.323
.001
Covariates
Salinity
1.265
1
2.265
44.392
.001
PBI
.510
1
.510
17.899
.001
Age of Seawater
. 182
1
.182'
6.386
.012
2-Way Interactions
14.007
89
.157
5.522
.001
Residual
7.952
279
.029
TOTAL
49.126
390
.126
362
-------
Table VIII-6. SIGNIFICANCE OF ANNUAL VARIATION IN ABNORMALITY AND-
MORTALITY (p = 0.001)* OF PACIFIC OYSTER LARVAE FOR
DATE AND STATION IN BELLINGHAM BAY FOR SURFACE WATER
SAMPLES
ABNORMAL DEVELOPMENT (%) OF LARVAE IN EACH YEAR
1972 1970 1969 and 1971 1968 1973 1976 1975 1974 1977
41 40 33 33 30 24 22 19 16 15
ABNORMAL DEVELOPMENT (%) OF LARVAE AT EACH STATION
1115 1417 1620 2217 2731 1644 3013 3926 3308
4115
¦ 3236
96 62 47 21 13 6 2 1 0
LARVAL MORTALITY (%) IN EACH YEAR
1974 1969 1977 1972 1971 1968 1970 1975 1973 and 1976
64 51 48 45 40 35 23 19 15 15
LARVAL MORTALITY (%) AT EACH STATION
1115 1417 1620 2731 2217 3013 3308 1644 4115 3926
3236
68 62 50 33 27 24 22 20 19 16
* Any mean not underlined by the same line is significantly
different at p < 0*001.
-36 3-
-------
Table VII1-7'. VARIATION IN RECEIVING WATER QUALITY AND TOXICITY TO OYSTER LARVAE IN
BELLINGHAM BAY, WASHINGTON-
SAMPLING
LOCATION AND DEPTH
(m)
Date of
01-1115
01-1417
01
-1620
01-2217
Bioassay
0
3.0
6.1
0
3.0
6.1
0
3.0
6.1
0
3.0
9.1
ABNORMALITY (%)
19 Jun 73
100
100
6B.59
100
2.78
0.06
100
0.05
0
1.38
0.73
0.07
25 Sep 73
100
100
100
100
11.09
0.0
31.56
1.02
0.34
76.38
72.35
0.01
4 Dec 73
58.27
83.31
99.68
50
96.41
0.11
0
0.42
0.14
99.47
0.11
0.25
6 Mar 74
50.00
100
99.67
71.3
0.35
0.0
0
0
0.17
22.46
0. 15
0.0
6 Aug 74
100
100
100
100
1.15
50.0
0
1.66
0
0.21
2.62
50.0
MORTALITY («}
19 Jun 73
100
100
57.78
87. 31
0.34
0.00
79.66
0
0
0.00
0.00
0.00
25 Sep 73
9.63
98.4
94.8
80.61
29.82
13.42
18.62
25.22
15.22
50.41
35.42
2.01
4 Dec 73
98.89
99.07
37.43
99.81
7.54
0.06
97.96
2.66
6.0
30.0
6.24
7.54
6 Mar 74
99.63
96.69
50.39
23.75
9.42
1.31
3.15
6.30
5.93
30.0
0.0
8.14
6 Aug 74
100
100
100
100
78.04
99.80
14.82
27.22
99.59
10.35
83.13
99.80
PBI (mg/1)
19 Jun 73
753
615
46
760
39
14
360
15
7
3
4
3
25 Sep 73
1555
355
71
51
23
0
24
17
0
9
0
0
4 Dec 73
135
390
52
0
37
12
31
16
2
38
4
0
6 Mar 74
11
252
36
20
7
0
14
9
3
22
8
3
.6 Aug 74
1560
1330
435
81
18
3
16
21
1
18
3
0
SALINITY (ppt)
19 Jun 73
10.3
25.8
29.1
22.1
28.0
29.5
22.10
28.7
28.9
30.0
29.6
30.2
25 Sep 73
17.9
26.9
29.3
28.4
28.7
30.5
28.6
28.9
30.0
29. 3
29.6
30.4
4 Dec 73
8.0
23.3
28.6
3.8
26.4
2h.l.
4.4
27.8
29. 3
|
17.2
28.9
29.6
6 Mar 74
7.6
23.0
27.5
18.6
26.9
2®rt» -
23.8
25.7
28.6 |
J
19.2
26.0
28.7
6 Aug 74
8.3
12.7
23.3
15.9
20.8
24.8
18.8
20.1
26.0 | 19.9
Continued
23.7
next page.
26.6
-------
Table VIII-7, page 2.
Date of
Bioassay
01-3013
SAMPLING LOCATION AND DEPTH (m)
01-2731 01-3926
3.0
9.1
0
3.0
6.1
0
3.0
9.1
100
1.05
0.0
0.72
0.25
0. 37
53.86
0.72
0.0
12.16
4.58
0.0
0.23
0.41
0.0
0.10
0.10
0.23
0.49
0.49
0.14
0.71
0.35
0.30
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
57.21
17.42
3.61
39.22
22.62
6.23
1.71
11. 38
10.51
0.0
2.28
5.07
0.94
9.58
0.0
6.09
0.94
1.50
55.48
93.49
48.97
70.73
80.69
16.24
I
u>
cn
Ln
I
ABNORMALITY( % )
19 Jun 73 0.03 0.03
25 Sep 73 0.28 0.21
4 Dec 73 0.43 0.37
6 Mar 74 0.18 0.0
6 Aug 74 0.0 0.0
MORTALITY (%)
19 Jun 73 0.0 0.0
25 Sep 73" 4.61 1.61
4 Dec 73 0.0 0.0
6 Mar 74 4.44 2.78
6 Aug 74 79.47 97.36
PBI (mg/1)
19 Jun 73 1 1
25 Sep 73 3 1
4 Dec 73 0 0
6 Mar 74 6 1
6 Aug 74 0 0
SALINITY (ppt)
19 Jun 73 29.5 29.8
25 Sep 73 30.0 29.8
4 Dec 73 28.9 29.5
6 Mar 74 26.2 28.4
6 Aug 74 24.9 25.5
I
I
i
I
0.02 j
0.0 |
0.11 J
0.18 {
0.0 j
0.0
3.83 j
0.0
6.67
I
I
I
I
I
61.17 |
l
I
I
I
I
i
I
I
•
l
i
I
I
I
l
i
i
I
I
I
1
0
0
1
0
30.4
30.5
29.6
29.1
26.9
59
0
1
6
7
23.3
29.8
30.0
28.6
23.9
17
0
1
4
3
28.4
30.0
30.0
28.7
24.9
4
0
1
1
1
30.2
30.4
30.0
29.3 .
27.6
5
0
0
0
3
28.90
30.2
29.6
29.8
24.2
3
0
0
0
1
29.8
30.2
30.0
29.6
26.6
1
1
0
1
0
30.4
30.5
29.8
29. 3
27.8
-------
Table VIII-8 VARIATION IN ABNORMAL SHELL DEVELOPMENT OF OYSTER
LARVAE AS A FUNCTION OF SEASON, LOCATION AND DEPTH
OF SAMPLING AS WELL AS PBI, SALINITY AND THE AGE
OF SEAWATER AT TESTING FOR SEVEN LOCATIONS IN
BELLINGHAM BAY (1973 -74).
Sum Qf Mean
Source of Variation Squares d.f. Square F-Value Significance
FACTORS
Date
.492
4
.123
5.098
.001
Station
19.228
6
3.205
132.818
.001
Depth
1.622
2
.811
33.608
.001
COVARIATES
Salinity
.023
1
.023
.042
.334
PBI
.168
1
.168
6.975
.010
Age of Seawater
.001
1
.001
.052
.820
2-WAY INTERACTIONS
Date x station
1.878
24
.078
3.243
.001
Date x depth
.801
8
.100
4.151
.001
Station x depth
3.222
12
.269
11.129
.001
3-WAY INTERACTIONS
Date x station x depth
4.532
46
.099
4.084
.001
RESIDUAL
2.509
104
.024
TOTAL
34.963
209
.167
-366-
-------
Table VIII-9. VARIATION IN MORTALITY OF OYSTER LARVAE AS A FUNCTION
OF SEASON, LOCATION AND DEPTH OF SAMPLING AS WELL AS
PBI, SALINITY AND THE AGE OF SEAWATER AT TESTING FOR
SEVEN LOCATIONS IN BELLINGHAM BAY (1973 - 74).
Source of.Variation
Sum of
Squares
d.f.
Mean
Square
F-Value
Significance
FACTORS
Date
8.878
4
2.220
550.66
.001
Station
9.997
6
1.666
413.372
.001
Depth
.859
2
.430
106.557
.001
COVARIATES
Salinity
1.575
1
1.575
309.672
.001
PBI
1.005
1
1.005
249.294
.001
Age of Seawater
.079
1
.079
19.660
.001
2-WAY INTERACTIONS
Date x station
1.543
24
.064
15.947
.001
Date x depth
.554
8
.069
17.169
.001
Station x depth
2.016
12
.168
41.679
.001
3-WAY INTERACTIONS
Date x station x depth
4.617
46
.100
24.899
.001
RESIDUAL
.419
104
.004
TOTAL
31.239
209
.149
-367-
-------
icant (p < .001) , amounts of the variation in abnormal shell
development, while the covariates were not significant. The
most important factors were station, depth and their two- and
three-way interactions, which accounted for 55%, 4.6%, 9% and
13%, respectively, of the variation.
The toxicity of the receiving water was signficantly lower
(p i 0.001) in March 1974 than, in all other quarters (Table
VIII-10). Stations 1-1115 and 1-1417 were consistently the
most toxic, while Stations 1-2217, 1-2731 and 1-1620 showed
intermediate toxicity. Stations 1-3926 and 1-3013 were least
toxic based on the abnormality criterion. The toxicity was
greatest at the surface (38%) while no significant difference
was found at 3 {20%) and 6.1 m (18%).
All factors, factor interactions and covariates accounted for
significant (p < 0.001) amounts of the variation in the mortal-
ity of Pacific oyster larvae. The most important independent
parameters were location and date and the three-way interaction
of location, date and depth, which accounted for 32, 28 and
15%, respectively, of the total variation in the mortality
response. Among the covariates only salinity explained a
notable amount of the total variation at 5%, while PBI and age
of the seawater explained only 3% and 0.3%, respectively. In
a number of cases the surface salinities were less than the
minimum level (20%) considered acceptable for the normal devel-
opment and viability of oyster larvae (Woelke 1968). This may
result in a more-than-additive interactive effect (Cardwell
et al. 1979).
The mortality criterion indicated that € August 1974 and 25
September 1973 had the highest respective toxicity of 72 and 30%
(Table VIII-10). The mortality responses for 4 December 1973
and 19 June 1973 were intermediate and 6 March 74 was lowest.
Comparison of the abnormality and mortality responses showed
that 6 March 1974 was least toxic and that responses were approx-
368-
-------
Table VIII-10. SIGNIFICANCE OF THE VARIATION IN ABNORMALITY AND
MORTALITY (p < 0.001)* OF PACIFICE OYSTER LARVAE
FOR DATE, STATION, AND DEPTH IN BELLINGHAM BAY.
ABNORMAL DEVELOPMENT (%) OF LARVAE FOR EACH DATE
25 Sep 73 19 Jan 73 6 Aug 74 4 Dec 73 6 Mar 74
32 29 24 23 17
ABNORMAL DEVELOPMENT (%) OF LARVAE FOR EACH STATION
01-1115 01-1417 01-2217 01-2731 01-1620 01-3926 01-3013
93 39 22 11 9 1 0
ABNORMAL DEVELOPMENT (%) OF LARVAE FOR EACH DEPTH
0 m 3m 6.1m
38 20 18
MORTALITY (%) OF LARVAE FOR EACH DATE
6 Aug 74 25 Sep 73 4 Dec 74 19 Jun 73 6 Mar 74
72 30 25 20 18
MORTALITY (%) OF LARVAE FOR EACH STATION
01-1115 01-1417 01-1620 01-2217 01-2731 01-3013 01-3926
83 41 29 24 20 18 17
MORTALITY (%) OF LARVAE FOR EACH DEPTH
0 m 3 m 6.1m
41 33 26
* Any mean not underlined by the same line is significantly different
at p ,< 0.001.
-369-
-------
imately equal for all dates except for 6 August 1974. Stations
1-1115 (83%0 and 1-1417 (41%) nearest the discharge point were
most toxic, followed by Station 1-1620 (29%). The least toxic
stations (1-3013 and 1-3926) had 18 and 17% mortality, respec-
tively. The toxicity criterion at the three depths sampled
showed a significant gradient from the surface of 41%, 33%,
and 26% at 0,3, and 6.1 m, respectively. It is apparent from
this analysis that the receiving water bioassays indicated
that considerable toxicity remained in Bellingham Bay after
primary treatment of the Georgia-Pacific sulfite mill
effluent had begun in 1973.
Pulpmili Strike; A strike of pulp and paper mill workers at
all Puget Sound pulp mills for about two weeks in the autumn
of 1964 presented a unique opportunity to bioassay water sam-
ples from Bellingham to Anacortes at a time when no PBI positivb
materials from these mills were entering marine waters (WoeIke
1972). The assumption was that if the offending "pollutant"
were removed from the environment, some predictable change
(usually better survival of some test animal) would take place.
The bioassays were conducted on water collected four and
twelve days after closure, and five days after resumption of
pulping operations. The results of this study are present in
Table VIII-11 and Figures VIII-21 and VIII-22.
In the Bellingham - Anacortes area, the PBI level at Station
1 fell from an annual average of 586 ppm to 5 ppm 12 days after
closure, and rose again to 62 ppm 5 days after resumption of
pulping operations. The percent abnormality which averaged
99.7% prior to closure fell to 0.2% 12 days after closure
and increased to 100% 5 days after re-opening of the mill
(Figure VIII-22). This study illustrates the rapid increase
in oyster larvae normality with removal of pulp effluent.
There appears to be a strong correlation between water toxicity,
PBI and pulpmili operations.
-370-
-------
Table VI11-11 EFFECT OF PULPMILL CLOSURE ON WATER QUALITY AND OYSTER LARVAE RESPONSE
IN THE BELLINGHAM - ANACORTES AREA
Station
Average from annual
surveys
4 days after closure
12 days after closure
5 days
after reopenned
PBI
Abnormal
PBI
Abnormal
PBI
Abnormal
PBI
Abnormal
01-1417
586.0
99.7
28.5
91.3
5.0
0.2
62.0
100.0
01-5037
17.5
36.3
2.5
6.6
0.5
0.5
270.0
100.0
01-2731
48.8
68.7
17.5
47.2
0.0
0.6
1.5
2.8
01-2217
34.0
39.1
6.0
8.3
0.5
0.2
0.5
2.3
01-1644
33.2
59.8
17.0
66.3
1.0
2.0
4.0
2.7
01-3236
16.1
21.9
18.0
51.0
0.0
1.6
0.5
2.7
01-3926
8.7
17.6
—
0.0
0.6
—
—
01-4629
4.5
2.5
—
—
0.0
0.8
—
—
01-3308
6.9
5.1
4.5
5.3
0.0
0.3
0.0
1.2
01-6529
2.3
4.9
5.5
11.8
3.0
0.9
4.0
1.4
01-5246
5.8
19.2
2.5
9.1
0.0
0.7
1.5
2.4
01-4115
2.6
1.7
—
—
0.5
0.2
—
—
Pearl Benson Index in ppm. Source: Woelke 1972
Abnormal - mean percent of abnormal larvae.
All salinities >20.00 °/oo.
-------
Moau^oi Riwc
Strait of
Georgia
Lumml Bay , /^junrat
iortlon
Baltmgham
Po/tag* ||ii]\wlK»
£ \*4t
i
tiMrt
I \ W;
i
Chuchanul Bap
PtMMAt Bay
\EHia tat.
Wildcat Cow*
San Juan
Islands
Samith Bay
Fidalao
100 200
150 300
thousands of fe«t
Figure VIII-21. STATIONS SAMPLED FOR FBI AND PERCENT
ABNORMALITY.
Sources Woelke 1972
372-
-------
r 100
E
o
e
A
<
•o
c
75-
50-
a. 25
0 -
Average PBI and
Per Cant Abnor-
mality From An-
nual Surveys. (19641
P A
1
PA PA
2 3
~.m all —
PA PA PA PA PA PA PA PA PA
4 5 6 7 8 9 10 11 12 Sit*
f 100t
E
1 754
a
<
e
50-
Four Days
After Closure.
5 25-
6
0-
|ioo-r
e
i 754
£
<
*
P A
1
I
** **
*~
PA PA
2 3
P A
4
PAPA
5 6
PAPA
7 8
PAPA
9 10
PA PA
11 12 Sit*
50-
e
a
a.
04
Twelve Days
After Closure.
6
8 9 10 11 12 sit*
£100 -r
Five
Days
After
Reopened.
Key
P
PHI Levels
A
Abnormality
~
Not Samplad
Figure VIII-22.
EFFECT OF PULP MILL CLOSURE ON WATER QUALITY AND
OYSTER LARVAE RESPONSE IN THE BELLINGHAI1-ANAC0RTES
AREA
Source: Woelke 1972
-373-
-------
D. BIOLOGICAL AND ECOLOGICAL
Although muck biological data exists on the Bellingham Bay
area (see Chapter VI), little of the information is compre-
hensive or recent enough to analyze for relationships to pulp
mill effluent. In Chapter III it has been pointed out that
effluents travel in a generally southwest direction from the
mill, impinging on eelgrass beds, waterfowl areas, and areas
utilized by fish and shellfish. A high diversity of benthic
life is present in areas near the mill itself, although that
density is apparently affected by effluent distributions near
Georgia-Pacific.
Figure VI-3 shows that phytoplankton concentrations (indicative
of the major source of biological productivity in Bellingham
Bay) are reduced substantially by increased SSL and related
effluent components. A decreasing exponential curve could
be fit to the data, although there is a considerable amount
of scatter, particularly at low SSL levels. From Table VI-3,
one can observe a large drop in primary productivity between
50 and 100 ppm SSL.
Zooplankton does not correlate well with SSL values in either
a positive or negative sense. The results are scattered and
are obviously strongly dependent on both station location and
time of sampling. Plankton patchiness also plays an impor-
tant role.
Diversity of benthic invertebrates decreases subtantially
from the outer Bay to the inner harbor area. From Figure VI-7
the mean diversity for Class A waters in the outer bay is
1.63. Diversity on the line dividing the outer bay and inner
harbor is 1.60 (only two stations); however, inner harbor
values are only 1.17, falling most sharply in the area of
Whatcom Waterway. There is also an indication that diversity
is low along the east shore of the bay south of the Georgia-
Pacific Mill, staying somewhat lower than normal to Post Point,
-374
-------
where mill effluent can be expected to mix with sewage efflu-
ents from the City of Bellingham. CH2M Hill data (see Figure
VI-9) tend to confirm that diversity is highest away from
the pollution sources of the mill and sewage outfall. Station
4, located off Point Francis, shows the largest biological
diversity, although this may be influenced to some extent by
favorable substrate and/or eelgrass beds.
Fish spawn and migrate in areas near the normal effluent
path. This data is particularly well known for salmon and
herring (see Section VI-F). Abundance data on fish is not
consistent enough over a long time span to draw any reliable
conclusions on effects of mill effluents or treatment processes
from the abundance data itself. Information on toxic and water
quality effects is discussed in VHI-B and C. Marine mammals
and birds occur in only scattered observations with insuffici-
ent abundances for numerical or statistical analysis.
-375-
-------
REFERENCES
Barnes, C.A. and C. C. Ebbesmeyer. 1978. "Some Aspects of Puget
Sound's Circulation and water Properties," IN: Estuarine
Transport Processes. B. Xjerfve {ed.). University of South
Carolina Press, Columbia, South Carolina. 331 pp.
Barnes, C.A., E.E. Collias, V.F. Felicetta, 0. Goldschmid, B.F.
Hrutfiord, A. Livingston, J.L. McCarthy, G.L. Tombs, M.
Waldichuk, and R.E. Westley. 1963. "A Standarized Pearl-
Benson, or Nitroso, Method Recommended for Estimation of
Spent Sulfite Liquor or Sulfite Waste Liquor Concentration
in Waters." Journal of the Technical Association of the Pulp
and Paper Industry. T5"; 347-551'. : "
Callaway, R.J., J.J. Vlastelincia, and G.R. Ditsworth. 1963.
Puget Sound Oceanographic Field Studies data Report: Everett
Bellingham, and Port Angeles, 1962-1963. Unpublished data
on file at the Environmental Protection Agency Corvallis
Environmental Research Laboratory, Corvallis, Oregon.
Cannon, G.A. 1973. Observations of Currents in Puget Sound, 1970'
National Oceanic and Atmospheric Administration Technical
Report ERL 26C-POL 17.
Cannon, G.A. and N.P. Laird. 1972. Observations of Currents and
Water Properties in Puget Sound, j.£*72. National Oceanic and
Atmospheric Administration Technical Report No. ERL-247 PO-13.
Cannon, G.A., N.P. Laird and T.L. Keefer. 1979. Puget Sound
Circulation; Final Report for FY 77-18. National Oceanic
and Atmospheric Administration Technical Memorandum No. ERL
MESA-40.
Cardwell, R.D. 1980, Personal Communication to Q.J. Stober.
Cardwell, R.D. and C.E. Woelke. 1979. Marine Water Quality
Compendium for Washington State. Washington State Department
of Fisheries, Olympia, Washington. 2 Volumes. 603 pp.
Cardwell, R.D., C.E. Woelke, M.I. Carr and E.W^ Sanborn. 1976.
"Toxicity of Marine Waters near Everett and Port Angeles,
Washington, to Larval Pacific Oysters in 1^75." 88 p. INs
Ecological Baseline and Monitoring Study for Port Gardner
and Adjacent Waters. A Summary Report for Years 1972-75.
Washington DOE 76-20.
Cardwell, R.D., C.E. Woelke, M.I. Carr. and E.W. Sanborn. 1979.
Toxic Substance and Water Quality Effects on Larval Marine
Organisms"! Washington State Department of Fisheries
Technical Report No. 45.
-376-
-------
Collias, E.E. 1971. Current Measurements in Puget Sound and
Adjacient Waters, July 1948 - November 1955. University
of Washington Department of Oceanography Technical Report.
No. 271.
Collias, E.E. and C.A. Barnes. 1962. An Oceanographic Survey of
the Bellingham-Samish Bay System. Volume I - Physical and
Chemical Data. University of Washington Dept. of Oceanography
Special Report No. 32. 138 pp.
Collias, E.E., C.A. Barnes, C.B. Murty, and D.V. Hansen. 1966.
An Oceanographic Survey of the Bellingham-Samish Bay System.
Volume II- Analyses of Data. University of Washington
Department of Oceanography Special Report No. 32. 142 pp.
Conomos, T.J. (ed.). 1979. San Francisco Bay: the Urbanized
Estuary. The 58th Annual Meeting of the Pacific Division/
American Association for the Advancement of Sciences. 493 pp.
Cox, J.M., C.C. Ebbesmeyer, D.B. Browning, J.M. Helseth, L.R.
Hinchey, and D.W. Thomson. 1979. Dispersion of Pulp Mill
Effluent in Port Townsend Bay and Vicinity. 51 pp.
Ebbesmeyer, C.A. and C.A. Barnes. 1980 (In press). "Control
a Fjord Basin's Dynamics by Tidal Mixing in Embracing Sill
Zones." Submitted to Environmental and Coastal Marine
Science.
Ebbesmeyer, C.C. and J.M. Helseth. 1975. A Study of Current
Properties and Mixing Using Drogue Movements Observed during
Summer and Winter in Central Puget Sound, Washington.
Final Report to the Municipality of Metropolitan Seattle.
81 pp.
Ebbesmeyer, C.C., J.M. Cox, J.M. Helseth, L.R. Hinchey, and D.W.
Thomson. 1979. "Dispersion of Pulp Mill Effluent in Port
Angeles Harbor and Vicinity." IN: History and Effect of
Pulp Mill Effluent Discharges, Port Angeles, Washington.
G.B. Shea (ed.).
Environmental Data Service. 1975. Monthly and Annual Wind
Distribution by Pasquill Stability Classes Star Program,
Bellingham, Washington!" U.S. Department of Commerce, Na-
tional Oceanic and Atmospheric Administration. On file at
the National Climatic Center, Asheville, North Carolina.
Hansen, P.V. andM. Rattray, Jr. 1966. "New Dimension in Estuary
Classification." Limnology and Oceanography 11:319-326.
Johnson, Bruce. 1980. Personal Communication to Jeffrey Cox,
Evans-Hamilton, Inc.
Murty, C.B. 1960. The Estuarine Nature of Bellingham Bay,
Washington. Department of Oceaography, University of
Washington. Unpublished manuscript.
- 377-
-------
National Ocean Survey. 1976. Puget Sound Approaches, Circula-
tory. Survey Data Report. Preliminary Phase through Phase
III.October 1963-April 1975. Office of Marine Surveys
Maps. Oceanographic Division. 104 pp.
0'Keefe, J.L. 1960. A Preliminary Current Survey of Bellingham
Bay, Washington. Department of Oceanography, University of
Washington. Term report for Oceanography 460. Unpublished
manuscript.
Pacific Northwest River Basins Commission, Meteorology Committee-
1968. Climatological Handbook, Columbia Basin States.
Volume III, Part A: Hourly data. 341 pp.
Seattle Marine Laboratories. 1974. Evaluation of the Adequacy
of the Scott Paper Company Submarine Outfall in Guemes Channel.
63 pp. :
Sternberg, R.W. 1961. Recent Sediments in Bellingham Bay,
Washington. Northwest Science 41(2):63-79.
Tollefson, Roger. 1969. Biological Investigation. Summary Report<
for the Puget Sound Pulp Timber Company. 72 pp.
U.S. Department of Commerce. 1963-1966. Tide Tables, High and
Low Water Predictions. West Coast of North and South America
including the Hawaiian Islands. U.S. Coast and Geodetic
Survey. U.S. Government Printing Office.
U.S. Department of the Interior. 1967. Pollution Effects of Pulp
and Paper Mill Wastes in Puget Sound. A Report on studies
conducted by the Washington State Enforcement Project.
FWPCA and WPCC, Portland, Oregon and Olympia, Washington. 474 pp.
Vagners, J. and P. Mar. 1972. Oil on Puget Sound: an interdis-
ciplinary study in systems engineering. Washington Sea Grant,
University of Washington Press, Seattle, Washington. 629 pp.
Walden, C.C. and D.J. McLeay. 1974. Interrelationships of Various
Bioassay Procedures for Pulp and Paper Mill Effluents. CPAR
Report No. 165-1. Canadian Forestry, Ottawa, Ontario.
Walden, C.C., D.J. McLeay and D.D. Monteith. 1975. "Comparing
Bioassay Procedures for Pulp and Paper Effluents." Pulp
Paper Mag. Canada 76:T13Q-T134.
Waldichuk, M. 1957. "Physical Oceanography of the Strait of
Georgia, British Columbia." Journal of the Fisheries
Research Board of Canada 14{3).
Washington State Pollution Control Commission. 1963. In-Plant
Survey of Georgia-Pacific Corporation, Bellingham, Washington.
December 9-11, 1^63. 11 pp.
-378
-------
Washington State Pollution Control Commission. 1964. In-Plant
Survey of Georgia-Pacific Corporation/ Bellinqham. Washington.
July 13-16, 1964. 6 pp. !
Washington State Pollution Control Commission. 1967. Pollution
Effects of Pul]3 and Paper Mill Wastes in Puget Sound: a ~
report on studies conducted by the Washington State enforce-
ment projectJ u.S. Department of Interior, Federal Water
Pollution Control Administration. 474 pp.
Webber, H.H. 1978. Studies on Intertidal and Subtidal Benthos,
Fish and Water Quality in Bellingham. Hurley College. r
Western Washington University, Bellingham, Washington. 78 pp.
Westley, R.E. 1957. Washington State Department of Fisheries
Hydrographic Data,Vol. II, No. 6: Physical and Chemical Data
North Puget Sound Hydrographic Trips, 1956-1957. Washington
State Department of Fisheries. 21 pp.
Westley, R.E. 1960. "A Summary of Recent Research by the Washing-
ton State Department of Fisheries on the Distribution and
Determination of Sulfite Waste Liquor (SWL)." IN: Reports on
Sulfite Waste Liquor in a Marine Environment an? Its Effect <
on Oyster Larvae. Washington State Department of Fisheries*
Research Bulletin No. 6.
Westley, R.E. and M.A. Tarr. 1959. Physical and Chemical Data
North Puget Sound Hydrographic Trips, 1958. Washington State
Department of Fisheries Hydrographic Data Vol. Ill, No. 1.
46 pp.
Westley, R.E. and M.A. Tarr. 1960. Physical and Chemical Data
North Puget Sound Hydrographic Trips, 1959. Washington State
Department of Fisheries Hydrographic Data Vol. Ill, No. 2.
22 pp.
Woelke, C.E. 1968. Development and Validation of a Field Bioassay
Method with the Pacific Oyster, Crassostrea gigas, Embryo.
Ph.D. Dissertation, University of Washington, Seattle, WA.
141 pp.
Woelke, C.E. October 1972. Development of a Receiving Water
Quality Bioassay Criterion Based on the 48 Hour Pacific
Oyster,(Crassostrea gigas) Embryo. Washington Department
or Fisheries Technical Report No. 9. 93 pp.
-379-
-------
IX. CONCLUSIONS
The Georgia-Pacific pulp and paper mill in Bellingham, Washington
installed secondary treatment (June 7, 1979) for effluent wastes
more than 11 months subsequent to the date required by federal
regulations and permits. During the intervening period, the mill
discharged primary treated waste to the nearshore area near Whatcom
Waterway (during the first 10 months prior to submarine diffuser
operation) and northern Bellingham Bay in general (for the entire
period). During the period July 1978 June 1979 the primary
effluent discharge
• violated daily average BOD requirements of the NPDES
permit,
• caused high effluent loadings in nearshore waters,
• caused violations of water quality standards, for
dissolved oxygen in the inner harbor,
• caused introduction of toxic substances into marine
receiving waters.
The violations and environmental effects caused by these dis-
charges might have been mitigated through aeration and treatment
by a secondary treatment system.
The dynamics of Bellingham Bay are such that water and effluent
generally move southward, though at times winds tend to trap
effluent in the northern Bay. Current patterns are changable
based on tide, river flow and wind, although typical patterns
carry pulpmill effluent either down the eastern shore, or in a
counter-clockwise movement along the western islands (Lummi,
Portage, Elisa). In general, at least the SSL component of mill
effluent tends to concentrate in surface waters. Water quality
violations observed are primarily DO violations and have histor-
ically been most severe in the inner harbor waters near the mill,
Data on water quality following secondary treatment installation
is, as yet, too sparse to evaluate any changes which may have
occurred. Dilution of the effluent plume has beenT calculated at
1:121 in the near field and 1:35,000 at distances of 15-20 km.
This is a slow dilution relative to other plumes.
-380-
-------
Georgia-Pacific effluents have been shown to be toxic to aquatic
life through bioassays of fish, fish eggs and oyster larvae. Data
in recent mill bioassays show compliance with permit limits
although older post-primary treatment bioassays show non-compliance.
Bioassay tests run by federal and state agencies show that toxicity
is still a significant problem in the receiving waters. It has
been shown that toxicity generally decreases with distance from
the Georgia-Pacific mill and that toxicity decreased with time
after an extended mill shutdown.
Biological resources occur in northern Bellingham Bay in consider-
able diversity and abundances. Many of these organisms occur in
the path of the effluent, including eelgrass beds, commercially
harvestable fish and shellfish, marine birds and marine mammals.
Although acute toxicity has been demonstrated for these organisms,
chronic and sublethal effects are sparsely documented. Subtle
but potentially significant effects on ecological foodwebs and
on the marine ecosystem as a whole have not been studied, although
some inferences can be made from existing literature. Analysis
of foodwebs in the vicinity of Bellingham Bay does suggest poten-
tial long-term detrimental effects on these systems.
-381-
-------
APPENDICES
-382 -
-------
APPENDIX A
SUMMARY OF CURRENT METER MEASUREMENTS IN ROSARIO
STRAIT AND ROSARIO APPENDAGE
AND
OBSERVATIONS OF DYE AND DRIFTING OBJECTS IN ROSARIO
STRAIT AND ROSARIO APPENDAGE
-383-
-------
Table A-i. sumiuhy of cuhkent nkkk NEASuuiWNTs
IN R0SAR10 STVAIT AND ROSARIO AfreHDAOi
kfirtact
Station
Depth
Net
Net
Total
Observation Period
Latitude
Longitude
(¦)
Velocity
Direct tuu
Variance
begin
duration
48® K-
122 W-
(cm «"')
(°T toward)
<«? a'M
date
(davb)
(mlnutes)
(utinuteti)
1. Coll Us
02
l.S
To abort
to be of value
7-19-60
0
41.5
33.1
et •!., 1966
02
25
N
7-19-60
0
41.3
33.1
M
\ .8
To short
to be of value
7-20-60
0
41.6
33.)
01
25
•i
7-20-60
0
B3
1
To ahort
to be of value
7-10-61
0.06
44.6
30.)
S3
2
H
7-10-61
0.17
44.6
30.3
B3
2
H
7-10-61
0.13
44.6
30.3
113
3
M
7-10-61
0.09
44.6
30.3
B3
3
N
7-10-61
0.13
44.6
30.3
B3
4
M
7-10-61
0.12
44.6
30.3
¦3
6
•1
7-10-61
0.12
44.6
30.3
•3
8
*1
7-10-61
0.11
44.6
30.3
B2
1
To abort
to be of value
7-11-61
0.31
44.3
32.9
B2
2
II
7-11-61
0.18
44.3
32.9
B2
2
U
7-11-61
0.23
44.3
32.9
B2
4
H
7-11-61
0.07
44.3
32.9
B2
S
N
7-11-61
0.29
44.3
32.9
B2
s
M
7-11-61
0.28
44.3
32.9
B2
10
II
7-11-61
0.23
44.3
32.9
*2
IS
H
7-11-61
0.07
44.3
32.9
B2
20
••
7-11-61
0.23
44.3
32.9
2. IM 196)
k
3.1
2.7
1H
.110
4-17-63
23
43.9
36.0
unpubildwd
A
3.1
4.2
127
.101
5-09-63
19
43.9
36.0
(Collias
1971)
B
3.1
4.3
165
.029
4-17-63
23
45.2
34.0
B
3.1
3.1
141
.026
5-09-63
19
45.2
34.0
-------
Table A-l
AmNUlX A (continued)
Station
Depth
(»)
Net
- Velocity
(cut n"')
Net
Direction
(°T toward)
Total
Observation Period
begin duration
date (days)
Uatllude
48° N-
(nilnutes)
Longitude
122° W-
(uiinutes)
C
3.1
15.1
211
.078
4-17-63
23
44.8
31.5
C
3.1
10.3
210
.023
5-09-63
19
44.8
31.5
0
3.1
14.5*
4-17-63
23
43.8
30.6
D
3.1
18.1*
5-09-63
19
43.8
30.6
E
3.1
21.1*
4-17-63
23
43.5
33.5
E
20.3
1.4
164
.005
4-17-63
23
43.5
33.5
E
3.1
27.6*
5-09-63
19
43.5
33.5
E
20.3
No Deployment
5-09-63
19
43.5
33.5
C
3.1
6.6
249
.078
4-17-63
23
42.1
35.5
C
20.3
2.9
151
.010
4-17-63
23
42.1
35.5
C
3.1
No Deployment
5-09-63
19
42.1
35.5
G
20.3
No Deployment
5-09-63
19
42.1
35.5
H
3.1
1.7*
4-17-63
23
42.1
33.5
11
20.3
No Deployment
4-17-63
23
42.1
33.5
II
3.1
41.0*
5-09-63
19
42.1
33.5
U
20.3
4.9
143
.021
5-09-63
19
42.1
33.5
I
3.1
No Deployment
4-17-63
23
42.1
31.7
I
20.3
No Deployment
4-17-63
23
42.1
31.7
I
3.1
3.6
095
.046
5-09-63
19
42.1
31.7
I
20.3
2.4
185
.015
5-09-63
19
42.1
31.7
J
3.1
No Deployment
4-17-63
23
40.0
34.6
J
20.3
2.9
089
.045
4-17-63
23
40.0
34.6
J
3.1
2.4
201
.048
5-09-63
19
40.0
34.6
J
20.3
2.3
354
.067
5-09-63
19
40.0
34.6
-------
Table A-l
APPENDIK A (coottnue4)
hbtutM Station
hftb
<»>
Mat
Velocity
fen •' )
Met
Direction
<<*T toward)
-fatal
Variance
tm* a"J)
Obaecvatton fetiod
begin duration
date (day#)
Latitude
48° M-
(mlnutes)
Longitude
122° N-
(wlnucea)
K
J.J
No Deployment
4-17-63
23
40.0
33.0
K
20.)
Mo Iteploywent
4-11-63
23
40.0
33.0
K
3.1
3.5
01B
.045
5-09-63
19
40.0
33.0
K
20.3
Ho Duplayaent
5-09-63
19
40.0
33.0
3. Tidal ISJO
2.5
24.97
276
.269
3-22-64
4.5
11.5
39.1
Current Table*
7.3
26.00
290
.268
3-22-64
4.5
31.5
19.1
(USCGS)
11.5
27.33
301
.26)
3-22-64
4.5
31.5
19.1
1575(a)
2.4
11.20
2*8
.017
5-21-61
4.1
20.7
35.1
7.3
16.11
265
.020
5-21-63
4.1
30.7
35.1
12.2
15.87
264
.018
5-21-63
4.1
30.7
35.1
1375(b)
2.1
9.64
262
.035
5-21-63
4,2
30.6
34.4
6.1
1.31
114
.015
5-21-63
4,2
30.6
34.4
10.4
2.21
064
.031
5-21-63
4.2
30.6
34.4
1575(c)
3.4
5.98
261
.016
5-21-63
4.2
30.7
33.9
10.4
6.98
202
.021
5-21-63
4.2
30.7
33.9
11. J
6.98
202
.021
5-21-63
4.2
30.7
33.9
1580
4.6
<2.0
200
.008
9-28-64
4
31.9
33.7
37.5
11.13
210
.047
9-28-64
4
31.9
33.7
1585
Data nut
available
1590
4.6
4.44
242
.007
4-24-64
4
35.0
34.7
14.3
4.44
220
.007
4-24-64
4
35.0
34.7
22.6
4.44
190
.007
4-24-64
4
35.0
34.7
1595
4.6
4.as
138
.009
9-28-64
4.2
38.9
34.1
43.3
4.as
160
.009
9-20-64
4.2
38.9
34 d
72.S
4.65
160
.009
9-28-6*
4.2
38,f
-------
Table A-l
APPENDIX A (continued)
Reference
Station
Depth
(a)
Nut
Velocity
-------
Table A-l
APfKNDIK A (continued)
Reference Slat Ion
Depth
Nut
Nut
Total
Obserwati
on Period
LaiItude
Uneltudis
<«)
Velocity
Direct ion
Variance
bug In
duration
48° N-
122° W-
(cm »"')
<°T toward)
(«2 a*2)
date
(daya)
(uiiuutus)
(uliiutes)
9a
5
14.9
200
.451
1-29-74
28.0
27.08
46.95
9a
5
24.1
190
.494
3-12-74
23.1
27.08
46.95
9a
20.1
22. 8
165
.355
3-12-74
23.1
27.08
46.95
10
36.6
5.5
265
.705
2-14-74
14.9
31.32
42.13
11
5
2.0
088
.886
2-15-74
16.9
33.65
44.85
11
23
6.4
111
.813
2-15-74
16.9
33.65
44.85
12
22
12.8
121
.771
2-15-74
18.7
34.00
39.60
IS
5
1.2
245
.558
3-06-74
14.9
37.29
45.00
15
23
8.3
252
.484
3-06-74
14.9
37.29
45.00
IS
56.7
8.7
221
.376
3-06-74
14.8
37.29
45.00
16
23
13.4
234
.623
3-20-74
15.6
36.01
38.99
16
54.9
12.4
219
.528
3-20-74
15.6
36.01
38.99
19
S
19.0
087
.437
3-02-74
14.8
39.85
42.93
19
73.2
12.1
100
.328
3-02-74
14.9
39.85
42.93
20a
S
14.0
035
.253
2-14-74
34.7
40.40
42.30
20a
5
11.3
035
.265
3-06-74
34.7
40.40
42.30
21
23
6.9
084
.127
3-03-74
15.9
40.87
41.30
21
91.4
5.5
.095
3-03-74
15.9
40.87
41.30
23
5
22.3
234
1.161
3-03-74
14.9
31.43
37.89
23
23.8
15.1
255
.822
3-03-74
15.0
31.43
37.89
-------
Table A-l
APfKNDIX A (continued)
Reference
Station
Depth
<•»)
Net
V« locIty
lem a" )
Net
Direction
(°T toward)
Total
Variance
fu.2 A
Observation Period
begin duration
date (davit)
Latitude ,
48° N-
(ininutes)
Longitude
122° H-
(uilliuteti)
6. NOS (data
9b
21.3
21.0
296
.062
9-02-75
20.5
27.13
46.93
uti file «(
9b
35.9
23.9
164
.273
9-02-75
20.5
27.13
46.93
NCAA - Sand
27.13
46.93
Point, llaah.)
9b
4.5
19.7
183
.358
10-4-75
16.3
9b
21.3
17.6
173
.330
10-4-75
16.3
27.13
46.93
9b
35.9
15.4
167
.256
10-4-75
16.3
27.13
46.9)
9c
4.5
5.30
305
.048
9-22-75
28.83
27.40
40.40
9c
8.5
7.87
256
.206
9-22-75
37.17
27.40
40.40
9c
21.3
12.14
242
.268
9-22-75
37.17
27.40
40.40
17
4.6
5.8
167
.071
3-21-74
16.0
38.60
38.80
17
21.3
11.5
155
.068
3-21-74
16.0
38.60
38.80
17
39.6
16.7
149
.064
3-21-74
16.0
38.60
38.80
18
5
10.7
038
.046
3-06-75
37.65
36.00
18
21
11.3
049
.036
3-06-75
37.65
36.00
18
82
9.2
035
.019
3-06-75
37.65
36.00
20b
21
11.1
064
.289
2-21-75
40.62
42.43
20b
5
10.7
056
.248
3-12-75
40.65
42.42
20b
21
10.3
058
.224
3-12-75
40.65
42.42
24
5
0.1
130
.024
3-05-75
40.50
36.05
45
5
16.2
145
.167
3-06-75
40.98
46.50
45
21
14.6
147
.156
J-06-75
40.98
46.50
4)
87
15.2
139
.134
3-06-75
40.98
46.50
4b
98
16.7
136
.054
3-04-75
44.02
48.12
47
21
17.1
349
.167
2-21-75
44.90
4i 77
*
Speed only, no direction.
-------
Table A-2.
OBSERVATIONS OP DYE AND DRIFTING OBJECTS
IN ROSARIO STRAIT AND ROSARIO APPENDAGE.
I
U>
10
0
1
Reference
Type of objects
observed
Observation
depth (in)
Number of
objects
observed
Observation
period
Remarks
1. Saxton and Young,
1948
2. Wagner and Ice,
1958
float
float
0.8
29 Sept;
S, 12, 13 Oct.
1948
3. Collias et al.,
a. drift sticks, poles
0.3, 3.7
18-20
July
1960
1966
10-13
July
1961
b. drogues
10, 20, 30
18-20
July
1960
10-13
July
1961
c. dye
0
8
Feb.
1961
Dye observations also
22
Mar.
1961
reported In Drlggers
23
Mar.
1961
(1964)
12
July
1961
4. Wash. St. Water
float
I
4-8
18-19
Oct.
1962
Poll. Control
Coon., 1967
5. Seattle Marine
Laboratories,
1974
6. Schumacher and
Reynolds, 1975
7. U.S. Army corps
of Engineers, 1977
8. Pashlnskl and
Charnell. 1979
drogues
drogues
droguea
drift cards
1, 10, 20 6
5.5 6
1.5 4
0 5000
14 Nov. 1973
10 Dec. 1973
6, 28 Feb.;
19 Har. 1974
19-21 Apr. 1977 On file at Seattle,
Wash. District Office
April 1976-
November 1977 .
-------
APPENDIX B
OBSERVATIONS OF WATER PROPERTIES
IN ROSARIO STRAIT AND ROSARIO APPENDAGE
-3 91-
-------
Table B-l SUMMARY OF hydrocraphic
SURVEYS SINCE 19AO
Reference
Parameters
observed
Number of
stations
p»r survey
Number of
surveys
Observation,
per lod
Remarks
1.
Benson et al. (1941)
2.
Benson et al. (1942)
3.
4.
5.
Puget Sound Pacific
Oyster Bulletin (1946)
SWL
23
4
Feb.-May 1946
In conjunction with
oyster bed Inspections
Saxton & Young (1948)
a) SWL
b) Temp, SWL
6
varies
2
5
9-10 Nov. 1948
Sept.-Nov. 1948
Be 11Ingham Samlsh Bays
Padllla & Fldalgo Bays
6.
Barnes et al. (1956)
7.
Knapman (1937)
D.O., Temp., SWL,
wind dir., vel.
61-65
71-75
hourly
3-24 Rov. 1957
8.
Vaguer et al. (1957)
Temp., Sal., D.O.,
SWL
29
6
June-July 1957
9.
Hash. St. Poll. Control
Coon. (1957)
SWL
7
June-Aug. 1957
10.
Vestley (19S7)
Tenp., Sal., D.O. ,
SWL. B. 0.0.
27
7
Sept. 1956-
Dec. 1957
11.
Johnson et al. (1958)"
SWL, 0.0., Chlorlnity
23 March 1958
12.
Johnson et al. (1958)b
SWL, P.O., Chlorlnity
7 April 1958
-------
Table
to
1
(continued)
Reference
Parameters
observed
Number of
stations
oer survey
Number of
surveys
Observation
period
Remarks
13.
Knapman (1958)a
D.O. , Temp., SWL
Wind-dir., vel.
9 Dec.-4 Jan.
1958
14.
Knapman (1958)'*
O.O., Temp., SWL,
Wind dir., vel.
61-65
71-75
hourly
13 Jan.-Feb.
1958
IS.
Ochler et al. (195B)
SWL
3 July 1958
16.
Weacley (1958)
Temp., Sal.
16
1951-1957
17.
Westley & Tarr (1959)
Temp., Sal.,
SWL, B.O.D. ,
Chlorophyll
D.O. ,
pv
31
13
Jan.-Dec. 1958
18.
Weatley (1960)
Sal., SWL, Temp.,
nutrient diet.
19.
Neatley & Tarr (1960)
Temp., Sal.,
SWL, P04
Chlorophyll
D.O. ,
31
7
Jan.-Sept. 1959
20.
Colllaa & Barnes
(1962)
Temp., Sal.,
SWL. PO4
D.O. ,
27
14
Nov. 1959-
Nov. 1961
21.
Le Mler (1962)
Temp., Sal.,
SWL
D.O. ,
4
5
Hay-June 1962
Also aalmon live-
box bloaasays
22.
Tollefaon (1962)
Temp., Sal.,
SWL
D.O. ,
1953-1961
-------
Table B—1 (continued)
Reference
Parameters
observed
Number of
stations
per survey
Number of
surveys
Observation
period
Remarks
23.
Callaway et al.
(1963)
Temp., Sal., 0.0.,
SWL
16-63
7
May-July 1963
Unpublished data
24.
Hash. St. Poll. Coon.
(1967)
Temp., Sal., 0.0.,
SWL, P04
17
16
Oct. 1962-
Oec. 1964
Also reported In
Bartsch et al. 1967
25.
CH2M Hill (1969)
26.
Colllss et al. (1970)
27.
Newman (1973)
Temp., Sal., 0.0.,
pH, Turbidity,
B.0.0. , Sulfides,
Suspended Solids.
C.O.D., Total
Mercury, T.O.C.
6
15
12-21 Nov. 1973
Whatcom Waterway
28.
Howry (1974)
Temp., Sal., P.O., 10
pH, B.0.0., Sulfides,
Suspended solids,
C.O.D., Turbidity,
Total Hg, T.O.C.
dally
May-July 1974
Whatcom, I & J Street,
& SquaIleum Waterways
29.
Seattle Marine
Laboratories (1974)
30.
Hebber (1975)
Temp., Sal.,
Turbidity
9
10
31.
CH2N Hill (1976)
Temp., Sal., 0.0.,
SWL, Nutrient
Bacteria,
Chlorophyll, Heavy
metala
12
75
July 1972-
Oct. 1975
-------
Table B—1 (continued)
Reference
Parameters
Number of
Number of
Observation
Remarks
observed
stations
surveys
period
per Survey
32. Brown and Caldwell
Inc. (1976)
33. Webber (1978)
Temp., Sal.,
D.O., pH.
Light trans-
mlttance
10
1
29 April 1976
Data Is confidential
34. Cardwell and
Hoe Ike (1979)
-------
APPENDIX C
AERIAL AND SATTELITE PHOTOGRAPHS
OF ROSARIO STRAIT AND ROSAR10 APPENDAGE
-396-
-------
Table C-l. AERIAL AMD SATTELITE PHOTOGRAPHS OF
ROSARIO STRAIT AMD ROSARIO APPENDAGE.
Source
Type of Photograph
Observation Period
1. U.S. Army Corp
Aerial black and white
Yearly surveillance flights
of Engineers
2. U.S. Bureau of
Aerial black and white
Unknown
Land Management
3. Baker et al. (1978)
Sattellte
Several years
4.- Feely and Lamb (1979)
Sattellte
Several years
5. U.S. Environmental
Aerial, color,
April-July 1973
Protection Agency
multlspectral
April 1979
-------
APPENDIX d
MONTHLY TEMPERATURE VERSUS SALINITY
Key for Figures d-1 throughd -5:
solid line Belli-ngham Bay
dash-dot line Strait of Georgia off Entrance
Island
dash Strait of Juan de Fuca at New
Dungeness NE
Sources: Collias and Barnes 1962, Collias 1970
-398-
-------
II
o
7-
IB0-400
JANUARY
00 ^
<*9 1*9 *%£.<> \
«i n » 1 . *
32
i i i
28
SO
SALINITY (V..)
26
O .
Ul
5
100-400
>
v00
™ M H f
ao n
B T i
i
4"iW» T« V
3^0 \
*>»
1^ V
FEBRUARY
SALINITY {%•)
24 tS
SALINITY (%•)
Figure D-l
-399-
-------
u
<
oc
w
a.
H 7
90 28 M
SALINITY (•/••)
»-
G
ui
§
5
£
I
MAY
Ui
H
SO
M
M
24
St
SALINITY C/..)
IS-
C' a-
n.
JUNE
,-Sw
ISO
to
38
90
ts
M
24
SALINITY (•/••>
Figure D?2
-4Q0-
-------
Figure D-3
-401-
-------
AUGUST
SEPTEMBER
«£"
l/TOO
*» 'm,
I
St
3°
SALINITY
Figure D-4
-4Q2-
-------
Ui
K
3
5 t-l
C
IU
CL
«oA°
»/» _
>50
#T9
'too
if"
».JS-
•eo
too
tBO-400
'•-•-no
•V»eo 80
-»io
OCTOBER
—r-
»
i
SO
¦—!—
ts
SALINITY <•/••)
NOVEMBER
SALINITY (*/••)
DECEMBER
SALINITY (•/••)
Figure D-5
-403-
-------
APPENDIX E
ACUTE TOXICITY BIOASSAY TEST METHOD
AND
STATIC-BIOASSAY TO EVALUATE INDUSTRIAL EFFLUENT TOXICITY
- 404-
-------
WASHINGTON STATE
DEPARTMENT OF ECOLOGY
July 1974
Acute Toxicity Bioassay Test Method
Preface;
The Acute Toxicity Bioassay Test Method was developed through the
cooperation of Northwest Pulp and Paper Association, National Air
and Stream Improvement .Council, individual pulp and paper company
representatives, Department of Fisheries, the Department of Game
and the Department of Ecology. This procedure was developed to
allow a wide range of individuals to be able to conduct the test
and was not developed as a research procedure. Test procedure
was developed to provide uniformity in testing to meet the bio-
assay permit requirement. Other testing procedure may be substi-
tuted to meet the requirement of each permit provided prior
approval is obtained from the Department of Ecology.
The frequency of testing will be determined on a mill by mill
basis. The type of production facilities and the type of controls
will be consideried in determining the frequency. Intensive testing
will be required during the initial period of the requirement,
after which time the testing frequency will be reviewed in light*
of the testing results.
The Department of Fisheries have agreed to supply fish at a
nominal price to industries affected by this requirement.
Test Procedure;
I. BIOASSAY DESCRIPTION - General
A. 96 Hour Static Bioassay
B. 1) One sample per test period
2) Triplicate test solutions per sample, duplicate con-
trols per test period.
II. BIOASSAY - Specifics
A. Test Fish
1) Test fish shall be a species of salmonid, or equiva-
lent as shown by testing of the effluents to demonstrate
a comparable sensitivity of the alternate species.
2) Weight of fish per test aquarium not to exceed 1
gm/1. Largest fish not to exceed 1.5 times the length
of the smallest fish.
3) Minimum of ten fish per test aquarium.
4) Stock fish are to be acclimated to dilution water for
at least 7-10 days prior to testing. Any unusual
conditions (e.g., pesticides, paint sprays, etc.) that
-405-
-------
fish are exposed to should be reported. During the
four days prior to test, deaths must not exceed 5%
among stock fish.
5) Test fish should not be fed 2 days prior to or during
test.
6) Test fish shall not be used for more than one test.
B. Diluent Water
A convenient acceptable fresh water.source. Same source
should be used for acclimation water sources.
C. Sampling and Storage
1) One composite or grab sample of effluent will be
collected for bioassay per test per effluent discharge
point.
2) If sample cannot be tested immediately, it must be
stored in a completely filled, stoppered container
at about 4°C. Sample must be bioassayed within 48
hours.
D. Test Aquaria
Suggested standard size and shape - 5 gallon capacity,
wide mouth cylindrical glass jars {10" dia., 18" height).
Each test aquarium should contain a minimum of 10 liters
of test solution.
E. Test Conditions
1) Sample pH shall be adjusted within the range of 6.5-
8.5, and bioassay conducted. Initial pH will be noted
if adjustment is required.
2) Temperature - 15+ 2oc or acclimation temperature water
supply.
3) DO must exceed 5 ppm - aeration of the test solution
may be done by any approved method - for example:
a) Inverted funnel technique.
b) Glass tube control rate.
4) Controls to be run concurrent with effluent test. Any
mortality in the control could obviate that test and
require a rerun.
5) At the end of each test day mortality must be recorded.
Any abnormal behavior or unusual conditions will be
noted and dead fish removed.
-406-
-------
PROCEDURAL DEFINITIONS
Note: These definitions were formed for the purpose of this
procedure and should be strictly applied.
Acclimation
Behavior
Bioassay
Effluent
Mortality
Test or stock
organism
Toxic or
toxicity
- The organism's adjustment to a change in an
environment.
- The integrated movement of the whole organism.
- A measurement of the effect, on living organisms
of the concentration of materials or parameters
present under stated conditions..
- An aqueous discharge into the receiving water.
- The point at which the vital life signs, such
as operculum and fin movement, stop.
- The living organism used or held in waiting for
a bioassay.
- A condition that either directly or indirectly
causes mortality to an otherwise healthy organi&nf'
-407-
-------
Washington State Department of Ecology
General Procedure
for Static-Bioassay to Evaluate Industrial Effluent Toxicity
Introduction
The purpose of the static limit-bioassay performed by the Department
of Ecology, Olympia Environmental Laboratory, is to evaluate the
effect of an effluent on the resident and migratory salmonid fishes
in our waters. Discharges from various industries change environ-
mental parameters of dissolved oxygen, temperatureand pH. Those
parameters are monitored physically in-situ, but the in-situ
toxicity of an effluent is much harder to determine.
The toxicity standards for Washington State require that 100 percent
of the salmonid fish tested survive a 65 percent concentration of
an industry's effluent for 96 hours. All of the physical parameters
of dissolved oxygen, pH and temperature are to be held within the
tolerance limits.of the test organism.
Methods and Materials
The basic procedure for the static limit-bioassay comes from several
sources: Howard and Walden, 1973; Doudoroff et al., 1951; Sprague,
1969; Glass, 1973; APHA, 1971; and Weber, 1973. From these
references the standards for the Water Quality Laboratory Static
limit-bioassay have been established. They are as follows:
A. TEST.SOLUTION
1. Dissolved oxygen must be greater than 7.0 ppm. Aeration
through glass tubing at the rate of approximately one
bubble per second.
2. pH must be between 6.5 - 8.0 adjusted using H2SO4 or NaOH,
3. Temperature 15.0OC +2.0 per 24 hour in waterbath.
B. TEST ORGANISMS
1. Salmonid fishes
2. Flesh ratio must not exceed 1 gm/liter of solution.
3. The longest fish must be less than 1.5 times the length
of the shortest fish.
4. Test fish must be acclimatized ten days before conanen-
cement of bioassay.
5. Fish to be used in test are not to be fed for two days
prior to start of bioassay.
6. During 72 hour pre-test period no more than 5 percent
mortalities may occur.
7. Mortalities are to be removed immediately.
C. DILUTION WATER
1. Convenient, acceptable freshwater source.
2. Zero ambient toxicity before effluent dilution.
408-
-------
TEST SAMPLE
1. 24 hour composite, if possible, or random grab.
2. If stored for any length of time, it must be in the dark
at 4°C.
CONTROL SOLUTION AND ORGANISMS
1. Physical parameters same as test solution.
2. No more than 5 percent mortalities.
3. Same criteria for acclimiation etc. for test organisms.
REPORTING PROCEDURE
1. Mortalities reported as number and time.
2. Physical parameters 1-2 times per 24 hour.
3. Species and source of test organisms.
4. Condition of test organisms before and after bioassay.
5. Average length and weight of test organsims..
-409-
-------
REFERENCES
APHA. 1971. Standard Methods for Examination of Water and
Wastewater"! 14th ed. p. 685. !
ASTM. 1977. Symposium on Aquatic Toxicology, 1st, Memphis,
Tennessee, 1976. S.TP 634.
Doudofoff, P., B.G. Anderson, G.E. Burdick, P.S. Galtsoff, W.B.
Hart, R. Patrick, E.R. Strong, E.W. Surber and W.M. Van Horn.
1951. "Bio-assay Methods for the Evaluation of Acute Toxicity
of Industrial Wastes to Fish." Sewage and Industrial Wastes,
Nov. 51, 23(11), :1380-97. ! ~~
Environmental Protection Agency. 1978. Methods for Measuring
Acute Toxicity of Effluents to Aquatic Organisms. EPA-600/
4-78-012. :
Glass, G.E. 1973. Bioassay Techniques and Environmental
Chemistry. Ann Arbor Science Pub. Inc. 400 pp.
Howard, T.E. and C.C. Walden. 1972. "Basic Bioassay Techniques."
PuljD and Paper Magazine of Canada, No. 10, T285-T289, Oct.
Sprague, J.B. 1969. "Measurement of Pollutant Toxicity to Fish;
Review Paper I-III." Water Research, Pergamon Press, 1969.
Vol. 3, pp. 793-821.
Weber, C.I. 1973. Biological Field and Laboratory Methods for
Measuring the Quality of Surface Waters and Effluents.
Office of Research and Development, U.S.E.P.A., Cinncinnati,
Ohio 45268, EPA-670/4-73-001.
-410
-------
APPENDIX F
RECEIVING WATER BIOASSAY RESULTS
AND SSL LEVELSj 1961-1978
Source: Cardwell and Woelke 1979
-411-
-------
^Mortality
^Abnormality
YEAR: 1961
Spent Sulfite Liquor IPBII (mg/ll
"Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1961. Salinity criterion > 20 ppt
applied.
-412-
-------
^5
<3
^Mortality
<3
Spent Sulfite Liquor iPBIl Img/I)
M * > «*>&** m* --
c
<•_. ®
^Abnormality
YEAR: 1962
*,
KEY:
O - 5% -19%
# - 20%-49%
• - >50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1962. Salinity criterion >20 ppt
applied.
-413-
-------
yuflii.3»wl'8Jwx
" w""'"
&
*A
<•**
^jtfxSf
0\
w Ifc »4« * ' Jtfi
(MMI
»v«* ^ik>'
mmsmm
^Mortality
Spent Sulfite Liquor (PBH Img/ll
^Abnormality
YEAR:1963
*
KEY:
O - 5% -19%
£ - 20%-49%
• - > 50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1963. Salinity criterion > 20 ppt
applied.
-414-
-------
mm
wm^i
vV
mm
mi0mm
^;<<-xvwr-ss50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1964. Salinity criterion > 20 ppt
applied.
-415-
-------
* v V*-* T V „ ~
tj * *
4.*^ ^ v\ -V. ^^n- ...
' *•*¦»**¦*»¦¦**»*~ S i »
* " * \rf WV ^
Mortality
~y-«*4 * "
Spent Sulfite Liquor tPBl) Img/ll
Abnormality
YEAR: 1965
KEY:
Q - 5%-19%
* - 20%-49%
• - > 50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1965. Salinity criterion > 20 ppt
applied.
-416-
-------
v.
'Vv X"> *« '' • ..
A^'i
v v - \> *!^+< <¦
B
f^M11
<» v '
fSsilllli
if
S><5^.^;.::> :> :"r:::%
0
^Mortality
iisiSii®iiSiiiSiii®iiiil®^®ii
mm
»*«l
6 w~ u* §¦&. „
A V -**- . . ~
-23
Abnormality
YEAR: 1966
*KEY:
O - 5%-19%
Sjc - 20%-49%
• - > 50%
Spent Sulfite Liquor IPBII Img/ll
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1966. Salinity criterion > 20 ppt
applied.
-417-
-------
% *
v*.
~Mortality
lilllilliililllllifW
2 '¦* ' ' -
Spent Sulfite Liquor IPB11 lmg/ll
Abnormality
YEAR: 1967
*KEY:
o - 5% -19%
£ - 20%-49%
• - >50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1967. Salinity criterion > 20 ppt
applied.
-418-
-------
¦• ' ' s/ ,
£ ' <
. . . .
»*&:•:•£::;:'-tt"sS:"'
, «»« *¦
^ijV/J^SWvVA
^Mortality
Abnormality
MMi
YEAR: 1968
„ O:
% , V<*'
Spent Sulfite Liquor iPBIi (fflfl/ll
f
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1968. Salinity criterion > 20 ppt
applied.
-419-
-------
;z . ->*. .
*0
4 »W^:-$g#S£
&
* /;-~r -»
1 *-
Vrf*. -„
o* >'¦ *yg^
*.£ - •
» * *\
** -^VBg
^Mortality
^Abnormality
YEAR: 1969
4**\W
Spent Sulfite Liquor IPBII Img/ll
^
Toxicity maps of oyster larvae responses and. SSL concentrations by
station in north Puget Sound for 1969. Salinity crtierion > 20 ppt
applied.
-420-
-------
¦6
f' \ '**.
^Mortality
^3
Abnormality
Spent Sulfite Liquor iPBIl lmg/ll
YEAR: 1970
*KEY:
O - 5% -19%
£ " 20%-49%
• - > 50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1970. Salinity criterion > 20 ppt
applied.
-421-
-------
^Mortality
^Abnormality
YEAR: 1971
Spent Sulfite Liquor iPBIl (mg/tt
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1971. Salinity criterion > 20 ppt
applied.
-422-
-------
ifSfll!
* » ** - t* * I
- J- * * :
^Mortality
^Abnormality
YEAR: 1972
Spent Sulfite Liquor [PBIl Img/ll
f ¦ :">
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1972. Salinity criterion > 20 ppt
applied.
-423-
-------
^4 20 ppt
I applied.
-424-
-------
^Mortality
^/>VV
Spent Sulfite Liquor iPBl! Img/ll
Abnormality
YEAR:1974
*KEY:
O - 5%-19%
# - 20%-49%
• ~ >50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1974. Salinity criterion > 20 ppt
applied.
-425-
-------
0
^Mortality
¦mi
^Abnormality
YEAR: 1975
*KEY:
O - 5%-19%
sjc-- 20% - 49%
• - > 50%
Spent Sulfite Liquor IPBI) fmg/ll
t ¦
[ toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1975. Salinity criterion > 20 ppt
applied.
-426-
-------
10
^3
tyy&si'
^Mortality
i?&il|p$i$
§§&
^3
Spent Sulfite Li.quor 1PBII lmg/ll
^Abnormality
YEAR: 1976
*KEY:
o -
5% -19%
20%-49%
>50%
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1976. Salinity criterion > 20 ppt
applied.
-427-
-------
- S&S* , s ,» 1
"Ossy- ,'; ¦ I
j*4* h\ty<
sg #•.
My:y
^ *
e»P
^Mortality
<*C» X
' * V:
^4^4^.; 4 :
^Abnormality
YEAR: 1977
*KEY:
o - 5% -19%
£ - 20% -49%
• - >50%
Spent Sulfite Liquor (PBII Img/ll
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1977. Salinity criterion > 20 ppt
applied.
428-
-------
o
vpSS*
v >,<=?««¦
Q
^Mortality
#>
^K'i-ll
C
J&y&WftS&SW
ia&SS&S':
SSi&S^Sg!
^Abnormality
YEAR: 1978
Spent Sulfite Liquor iPBIl Img/ll
Toxicity maps of oyster larvae responses and SSL concentrations by
station in north Puget Sound for 1978. Salinity criterion > 20 ppt
applied.
-429-
-------
APPENDIX G
PLANKTON DATA
-430-
-------
NMkuexmvw
Strait of
Georgia
Lummi Bay
bammc
Indian
FKatton
I
t.\. ''
111
Area B-l
BetJingftam
Portag*
isi.
i m®
Chuckanut Bay
Pleasant Bay
Area B-ll
1 Eliza IsL
3--- /
/
H1.19M
I VJ&x*:::
I
/
/ Area S-ll^
S Area S-l
Samisti Bay
San Juan
Islands
Vandovi
Isl.
Pidalgo
Ariaeoriea
100 200
50 150 300
thousands of feet
Figure G-l PHYTOPLANKTON SAMPLE AREAS IN BELLINGHAM BAY FROM
MARCH 1959 TO JULY 1961.
Source: Tollefson 1962
-431-
-------
TABLE G-l , PUNKTON COMPOSITION - WATER SAMPLES
Percent of Total Per Group* By Area
(From. Squally TFeignted Monthly Ifeans)
See Figure G-l , Source: Tollefson 1959
Area
Area
Area
Area
Area
All
B-I
B-II
B5-IT
S-II
S-I
Areas
PHITOELANKTON
Uelosira
29.51 %
33.50 %
35.50 %
1*3-91 %
18.13 %
33.121 %
Stephanopyxis
0.00
0.01
0.00
o.oi*
.0.12
0i03
Skeletonema
19.05
10.1*2
1».67
5.76
0.63
7.50
Thalassiosira
22.50
28.15
ia.75
20.55
9.87
26.11
Coscinodiscus
1.73
1*.1*2
2.80
3.67
3.18
3.23
Planktoniella
0.06
0.01
0.00.
0.02
Trace
0.02
Chaetocercs
2.32
3.13
2.10
5.28
1.38
2.91
Ditylum
0*05
0.01
0.01
0.01
Trace
OiOl
Biddulphia
0.97
0.92
1.03
0.90
1.68
1.08
Tabellaria
0.08
0.23
0.16
0.36
2.38
0.59
Striatella
0.03
0.08
0.00
0.08
0.1*7
0.12.
Licmophora
0.06
O.lil*
0.13
0.51*
1.89
0.57
Fragilaria
1.07
0.7U
0.61*
0.89
0.97
0.83
Asterionella
U.11
0.05
0.05
0.25
0.00
0.67
Thallasiothrix
0.1*7
0.1*1*
0.08
0.12
0.01
0.21
Achnanthes
0.01
0.01
0.00
0.01
0.06
0.02
Cocconeis
0.20
0.52
0.27
1.88
U.36
i.S
Navicula
U.52
9.1x0
7.71*
9.78
1*2.22
13.51
Fleurosigma
0.05
0.28
0.1*1
0.20
0.97
0.38
Nitzschia
12.90 .
7.21
2.66
5.72
11.68
7.29
Miscellaneous
0.01 •
0.03
0.00
0.03
0.00
0.01
100.60 %
lOBTEC %
10O5 % ltiCuoo %
100.06 %
10OTJ %
PROTOZOA.
Silicoflagellates 1.32 %
Ciliates 93.93
Tintinnida k»7$
1(305 %
1*.62 %
91.82*
3.51*
100.CO %
26.96 % 8.76 %
67.37 71.80
5.67 19.1*1* -
100.00 % 106.x %
18.62 %
57.87
23.51
1553 %
8.98 %
82.20
8.82
105T55 %
ZOOPLANKTCN
Coab Jellies
0.08 jf
0.19 %
0.00 %
0.02 25
0.C0 %
0.06 i
Jellyfish
o.i*o
0.61*
0.08
1.01
0.1*2
0.1*6
Flatwoims
0.93
1.59
O.36
3.1*
2.5U
1.66
Nematodes
0.65
1.61
0.19
1.66
1.12
1.00
Annelids
2.15
7.05
9.86
5.13
U.57
6.01
Cladocera
2.60
U.07
1.09
2.53
0.61
2.08
Copepod Nauplii
38.67
39.58
1*8.61
1*0.05
55.61*
1*5.1*7
Copepods
31.32
20.15
13.33
25.81*
23.3?
22.00
Barnacle Na-aplii
1.63
3.59
0.88
1.3k
1.78
1.89
Barnacle Cyprls
0.32
0.88
0.30
0.21
0.25
0.1*1
Crab 2oea
0.07
0.1*0
0.18
0.21
0.26
0.23
Crab Megalops
0.08
0.Q3
0.00
0.02
0.00
0.03
Gastropod Larvae
0.09
0.20
0.03
0.22
0.12
0.12
Bivalve Larvae
0.05
0.Q3
0.03
0.00
0.Q3
o.ol*
Bryosoa Larvae
0.08
O.38
0.05
0.08
0.03
0.13
Arrow Worms
2.07
0.03
0.00
0.00
0.00
0.36
Starfish Larvae
0.00
3.15
2.1*6
1.1*8
0.30
1.51*
Timicates
18.60
16.18
22.1*0
16.17
8.76
16.26
Miscellaneous
0.21
0.25
0.15
0.57
0.20
0.25
100.00 %
100.00 %
100.00 % 100.00 %
1TO35 %
100.00 %
-432-
-------
TABLE G-2 , GENERAL SUMMARY OF MEANS (x) AND STANDARD DEVIATIONS (S)
HYDROGRAPHIC FACTORS AND PLANKTONIC (LOGARITHM) VALUES
By Season and Area - By Method of Stucfy
See Figure g-1 '
Source:
Fall x
S
Winter x
S
Spring 1 x
S
Spring II x
S
OJ
Gj
I
Summer
B-I
B-II
BS-II
S-II
S-I
TOTAL
x
S
x
S
x
S
x
S
x
S
x
S
x
S
Sal.
o/oo
27^5
2.51
26.76
2.71
25.37
U.66
25.16
3.1*1
2l*.75
I1.28
22.17
$.09
25.61
2.80
26.81
3.32
27.83
1.69
26.97
1.36
25.87
3.67
GRAB WATER SAMPLES
Tollefson 1959
SESSILE FORMS (SETTING SLIDES)
Temp.
°C
12.08
1.61
7.13
0.92
7-61*
0.99
11.67
1.71
15.96
2.31
11.1*9
U.59
10.96
3.76
10.18
2.91
10.76
3.21
11.00
1*.18
10.88
3.76
SSL.
EEL
26.9
33.8
1*0.8
56.7
175.3
370.1
158.6
282.8
77.0
99.9
333.li
31*0.6
37.U
16.7
17.u
15.1
9.3
8.7
8.1
6.8
89.8
206.6
Protozoa
Hundreds*
1.014
0.69
1.11
0.66
1.19
0.78
1.32
0.62
2.1*0
0.60
1.86
0.70
1.7U
0.68
1.1*9
0.90
1.67
0.90
1.11
0.96
1.62
0.83
Phyto-
plankton
Thousands*
1.67
0.1*1*
i.5o
0.35
1.77
0.35
2.5U
0.28
2.61
0.U9
1.86
0.61*
2.00
0.65
2.02
0.69
2.12
O.63
2.08
0.1*5
2.01
0.62
Sal.
0/00
28.20
1.1*5
26.36
2.93
25.91
3.61
2l*.6t*
3-1*6
23.01*
It.80
22.87
li.70
25.58
2.73
28.22
1.29
25.1*6
3.82
Temp*
°c
12.52
0.81
7.11
0.1*8
7.69
1.11
12.05
1.50
16.31
2.31
11.39
U.U7
IO.83
3.79
10.81
3-1*7
11.00
3.87
SSL.
EEL
37.3
1*8.2
51 .1*
63.1
131.6
263.3
239.8
368.8
71.3
72.2
266.8
300.2
35.1*
17.3
8.0
7.0
102.0
203.0
Protozoa
JW
mm"
1.92
1.11
1.1*0
0.91
1.1*5
1.13
1.1*8
0.96
1.88
0.66
2.1*8
0.70
1.31
0.66
1.03
0.80
1.61
0.93
Phyto-
plankton
Jl ~
mmc
1.97
0.68
1.18
0.11*
1.7U
O.Ul
2.25
.0.1*1*
2.26
0.67
1.58
0.35
1.89
0.58
2.11*
0.73
w
S I
S II
B-I
B-II
BS-II
S-II
1.93
0.65
TOTAL
TOTAL
LESS B-I x
S
«Nvunbers /3>5L
26.52 12.01 21.7 1.19
2.21 3.60 26.5 0.73
NOTE* Values may vary slightly from those shown depending upon
exact analysis involved, due to differentials in N»
2.00 TOTAL
0.68 LESS B-I
-------
APPDENDIX H
SPECIES LIST OF INVERTEBRATE ORGANISMS
-434-
-------
Table H-1 SPECIES LIST. OF INVERTEBRATE ORGANISMS IN BELLINGHAM
BAY (Source: Webber 1977).
Phylum Annelida „ , . . , . _
— Lumbwnerezs bzfurcata
Ammotrypane aulogaster
Lurribrinereis zcmata
Armandia brevis
Maldane glebiflex
Artaaama conifera
Maldane sarai
Asychia aimilia
Mediomaatua ambiaeta
Axiothella rubrocineta
Melinna criatata
Capitella aapitata
Miaropodarke dubia
Caulleriella gracilis
Myxicola sp.
Cerebratulua californienais
Neanthea brandtl
Chaetozone setoaa
Nephtya califozmien8i8
Chone sp.
Nephtys eornuta
Cirratulue cirratna
Nephty8 eornuta franciaiana
Cirratulidae sp.
Nephyta longoaetoaa
Ctenodrilna sp.
Nereia sp.
Dorvillia sp.
Notkria elegana
Dorvellia rudolphi
Notoma&tua tenuis
Enchtraeidae
Oligochaete
Etonone sp.
Onuphia sp.
Eteone longa
Ophiodromua pugettenaia
Eudistylia vancouveri
Ouenia fuaifonrria
Eudorella sp.
Oxyoroatylis
Eulalia sp.
Parapriono8pid
Eunice kobiensis
Paronella platybrccnohia
Glycera nana
Paronella spinifera
Glycinde armigera
Pectinaria belgica
Glycinde picta
Pholoe rrrinuta
Gyp-tia brevipalpa
Phyllodoce caatanea
Ealo8ynda breviaetosa
PLata sp.
Halo8ynda insignia
Polyeunoa tuta
Harmothoe irribricata
Praxillella gracilis
Hemipobua borealia
Priabulua caudatua
Beteromaatua filobranchua
Prionospio pinnata
Laetmonice pellucida
Prionoapio ateenatruppi
-435-
-------
Table H-l Continued (page 2).
Protodorvillia gracilis
Paeudopolydova Kempi japonica
Saccooirrua eroticua
Scalibregma inflation
Spiophanee banbyx
Spiophane berkeleyrwn
Sternapaia foasor
Syllidae
Telepsavus oostarum
Tereb elHdes atroemi
Tharyx multifilia
Thelepua orispus
Thelepua setosua
Phylum Arthropoda
Anatonis mormani
Archaeomy8i8 grebnitzkii
Balanus glandula
Balanus crenatua
Calianas8a sp.
Cancer oregonensis
Cancer magister
Cancer productua
Chianocetea bairdi
Colurostylis sp.
Crogo fancisoorum
Crangon sp.
Gnori8maahaeroma oregonensia
Semigrapsus nudua
Hemigrap8UB oregoneais
Eeptioarpua sp.
Bippolyte clccrki
Syas lyratuB
Idotea aculeata
Idotea reaeaata
Lophopanopeus bellua
Ovegonia gracilis
Pagurua sp.
Pandualua sp.
Paracrangon eohinata
Petrolisthes oinctipes
Pirmixa occidentalis
Pinnixa schmitti
Pugettia gracilis
Pugettia richii
Hhizaaephala sp.
Spirontoaaris paludiacola
Spriontoaaris piota
Spi rontoaaria
Telmeaaua eheirogonua
Phylum chordata
Aacidia paratropa
Aaoidiacea sp.
Bo I tenia viIlosa
Corella willmriana
Pyura hauator
Phylum Cnidaria
Anthopleura xanthogramnriaa.
Metrodium senile
Metoidium marginatum
Ptilo8arcue gurneyi
Tealia oraasiaorni8
Virgularia sp.
Phylum Ctenophora
Ctenophoran sp.
Pleuobrachia bachei
-436-
-------
Table H-l Continued (page 3).
Phylum Echinodermata
Amphioda occidentalis
Cuaumaria miniata
Cucwnaria piperata
Crossaster papposus
Dermasterias inbrioata
Eupentaota quinque semita
Leptasterias hexaotia
Leptosynapta clarki
Luidia foliolata
Ophiura sarsi
Para8tiohopue oalifornicus
Piaaster brevispinus
disaster oohraoena
Pycnopodia helianthoides
Solaster stimpaoni
Strongelocentrotua s p.
Phylum Mollusca
Aoila oastremsis
Acmaea sp.
Aoteoaina ouloitella
Ampfiiasa colwrbiana
Anieodori8 nob-ilia
Armina oalifornioa
Axinopsida serrioata
Balanus glandula
Bankia setaaea
CaVLiostoma sp.
Calyptrea fastigiata
Cardiomya oalifornioa
Cardita venucoaa
Chlanys herieius
Clinooardium blandum
Collisella digitalis
Cotus sp.
Compsomyax subdiaphana
Corphium sp.
Creiodula sp.
Cyliohna alba
Cylidhna attonsa
Cyolocardia sp.
Dendronotus s p.
Diavlula sandiegensis
Doridaoea sp.
Entodeama saxioola
Fuatiaria reotius
Gastorpteron pacificum
Gastropteron sp.
Hermissenda araaaioomia
Bipponix sp.
Kellia laperouai
Lacuna aarinata
Liocyma scammoni
Littorina sautalata
littorina sitkana
Lophopanopeum bellue
Lyortsia oalifornioa
Maooma balthioa
Maooma brota
Maooma inoonspioua
Macoma inquinata
Maaaoma naauta
Maooma aeota
Maooma yoldiformia
Meroenaria kenniaotti
Mitrella gouldii
Mopalia intermedia
-437-
-------
Table H-l Continued (page 4).
Naculana hamata
Naaula tennis
Na&aarium cooperi
Naaaarins mendiaus
Notoacemea scutum
Nuculana hamata
Nuculana minuta
Pagurua sp.
Pandalua sp.
Femora filoaa
Pandora grandis
Pectin aavrinus
Pectin hericua
Pododeamus cepio
Pododeamum mousroachiamo
Potinioea levriaii
Proteothara staminea
Paephidia lordi
Pugettia gracilis
SaxLdomia giganteua
Spirontocaris paludicola
Spirontocaris piata
Spirontocaria s p.
Tellina bogogenais
Te lme88U8 cheiragonua
Thais lamello8a
Thaia sp.
Traaellnella tantilla
Trichotropi8 cancellccta
loldia limitula
loldia aciasorata
Mu8cuius laevigatus
My a arenaria
My sella tumida
Mytilua edulis
Phylum Nemertea
Cerebratulua sp.
Nemertea sp.
Paranemertea peregrina
-438-
-------
APPENDIX J
SHELLFISH BEDS
-439-
-------
Figure 'J-l SHELLFISH BEDS IN THE BELL INGHAM BAY REGION
Source: Goodwin and Shaul 1978
Market size
All sizes/
Location &
Station
Water
clams/sq.ft.
SQ.
ft.
depth
Butter
Uttleneck
Horse
floure no.
no.
ft.
No.
Wt.
No.
Wt.
No.
Wt.
Substrate tvoe & cover
Hale Passage
1
8
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
(see Figure
2
15
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
3
14
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
J-l)
4
6
0.0
0.00
0.0
0.00
0.0
0.00
sand
5
5
0.0
0.00
0.0
0.00
0.0
0.00
4* sand over shell, pea
gravel
6
20
0.0
0.00
0.0
0.00
0.0
0.00
mud
7
19
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
a
24
0.0
0.00
0.5
0.06
0.0
0.00
15" sand, gravel over mud
9
17
1.0
0.32
0.0
0.00
0.0
0.00
mud, sand, pea gravel,
gravel, shell
10
11
0.0
0.00
0.0
0.00
0.0
0.00
4* mud, sand over clay
11
20
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
12
12
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
13
12
2.5
0.60
0.0
0.00
0.0
0.00
mud, gravel, shell
14
12
0.5
0.39
2.5
0.19
0.0
0.00
gravel, boulders
15
5
...
...
...
...
...
sand, boulders
16
9
0.5
0.35
4.5
0.63
0.0
0.00
mud, pea gravel, gravel,
shell, boulders
17
22
1.0
0.48
1.5
0.09
0.0
0.00
pea gravel, gravel, boulders,
shell
18
13
0.5
0.29
3.0
0.20
0.0
0.00
6" mud, gravel over clay,
boulders
19
15
0.5
0.20
2.5
0.25
0.0
0.00
mud, sand, pea gravel, gravel,
boulders, shell
20
9
0.5
0.07
0.0
0.00
0.0
0.00
12" mud, sand over shell
21
15
0.0
0.00
0.0
0.00
0.0
0.00
mud
22
11-9
...
...
...
...
...
...
pea gravel, gravel, shell
23
14
0.0
0.00
0.0
0.00
0.0
0.00
gravel, boulders
24
15
0.0
0.00
0.0
0.00
0.0
0.00.
gravel, boulders, shell
25
35
0.0
0.00
0.0
0.00
0.0
0.00
mud, pea gravel, gravel,
shell
26
21
0.0
0.00
0.0
0.00
0.0
0.00
sand
27
7
0.0
0.00
0.0
0.00
0.0
0.00
sand
28
16
0.0
0.00
0.0
0.00
0.0
0.00
sand, shell
29
10
0.0
0.00
0.5
0.07
0.0
0.00
sand, gravel, shell
30
13
0.0
0.00
0.0
0.00
0.0
0.00
sand, gravel, shell
31
8
0.5
0.2B
2.0
0.2S
0.0
0.00
pea gravel, boulders
32
16
0.0
0.00
0.0
0.00
0.0
0.00
sand, gravel
33
17
1.0
0.21
3.5
0.32
0.0
0.00
mud, sand, gravel, shell
34
16
0.5
0.12
0.0
0.00
0.0
0.00
mud, sand, gravel, shell.
boulders
35
19
0.5
0.15
0.0
0.00
0.0
0.00
12" mud, sand, gravel, shell.
boulders over clay
36
20
0.5
0.11
T>.5
0.04
0.0
0.00
12" mud, sand, gravel, shell
over clay, boulders
37
22
1.5
0.51
0.0
0.00
0.0
0.00
12" mud. sand, gravel, shell
over clay, boulders
38
26
0.5
0.11
1.0
0.03
0.0
0.00
mud. gravel, shell
(Continued
440
-------
Figure J—l, Pg. 2
Location &
fiqure no.
Station
no."
Water
depth
ft.
Harket size
dams/sQ.ft.
All sizes/
sq.ft.
Substrate type & cover
Butter
Uttleneck
Horse
No.
Ut.
NO.
Ut.
No.
wt.
Hale Passage
(cont.)
Bel 11ngham
Bay
(see
Figure J-]
Sinclair
Island
(see
Figure
J-2)
Gu ernes
Island
(.see
Figure
J-21
39
40
41
42
43
44
45
46
47
48
49
50
1
2
3
> 5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
1
2
3
4
5
6
7
8
9
10
11
1
2
3
4
5
6
7
8
9
10
11
12
13
14
20
27
25
19
25
22
27
18
20
18
19
11
17
11
16
18
14
43
37
34
29
23
23
31
29
30
34
37
38
30
36
36
42
11
18
18
13
18
23
7
30
20
20-50
40-50
26
50
25
55
55
50
28
5^
52
20
30
25
21
11
0.0
0.0
0.0
0.0
1.0
0.5
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
d.o
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.5
1.0
0.0
0.0
0.0
1.0
1.5
3.0
2.0
1.0
1.5
0.5
2.5
4.0
0.5
0.5
1.0
0.5
0.0
0.0
0.0
0.5
0.0
0.00
0.00
0.00
0.00
0.25
0.11
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.17
0.24
0.00
0.00
0.00
0.50
0.74
0.68
0.50
0.19
0.25
0.13
0.36
0.63
0.09
0.17
0.15
0.00
0.00
0.00
0.12
0.00
0.0
0.0
0.0
0.0
1.0
0.5
0.0
0.5
0.0
0.0
0.0
0.0
0.0
0.0
0.5
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.5
2.5
0.0
0.0
0.0
0.0
0.0
0.0
0.5
0.5
0.0
0.0
1.0
0.0
0.5
0.0
0.00
0.00
0.00
0.00
0.06
0.03
0.00
0.04
0.00
0.00
0.00
0.00
0.00
0.00
0.02
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
o.oo
0.00
0.00
0.00
0.00
0.04
0.22
0.00
0.00
0.00
0.00
0.00
0.00
0.04
0.03
0.00
0.00
0.03
0.00
0.03
0.00
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
o.oo
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
mud, gravel, shell
mud, gravel, shell
mud, pea gravel, gravel, shell
sand, pea grjvel, gravel,
shell, boulders
sand, pea gravel, gravel, shell
mud, pea gravel, gravel, shell
mud, pea gravel, gravel, shell
pea gravel, gravel, boulders,
shell
sand, gravel, boulders
sand, gravel, boulders
sand, pea gravel, gravel, shell
sand, pea gravel, gravel, shell
mud
mud, sand, gravel, shell
pea gravel, gravel
mud
mud
mud
mud, wood chips
mud, wood chips
mud
mud, wood chips, debris
mud, wood chips >
mud, wood chips
mud, wood chips
mud, wood chips
mud, wood chips
mud, wood chips
mud, debris
mud, wood chips
mud
1/2" mud over sand, gravel
1/2" mud over sand, gravel
mud, clay, sand
pea gravel, gravel, clay,
boulders
pea gravel, gravel, clay,
boulders
mud, sand
sand, pea gravel, gravel
gravel, shell
sand, gravel, pea gravel
sand, gravel, pea gravel,
boulders
mud, pea gravel, gravel, shell,
rock outcropplngs
rock outcropplngs
rock outcropplngs
sand, gravel, shell
sand, gravel, shell
pea gravel, gravel, boulders,
clay
sand, pea gravel, gravel, shell
sand, gravel, shell
sand, pea gravel, gravel, shell
mud, pea gravel, gravel,
boulders
nud, sand, gravel
mid, sand, gravel
sand, pea gravel, gravel
gravel, shell
nud, gravel
nud, pea gravel
nud. sand
(Continued)
441tv
-------
Figure J-l, Pg. 3
Location &
floure no.
Station
no.
Water
depth
ft.
Market size
clams/sa.ft.
An s'izes/
sq.ft.
Substrate tvoe & cover
Butter
Llttl
eneck
Horse
No.
wt.
No.
Wt.
No.
Wt.
Guemes
15
23
0.0
0.00
0.0
0.00
0.0
0.00
mud. sand
Island
16
22
2.5
0.61
0.0
0.00
0.0
0.00
mud, sand, pea gravel
(cont.)
17
21
0.5
0.25
0.0
0.00
0.0
0.00
sand, shell
18
20
1.0
0.45
0.0
0.00
0.0
0.00
mud, sand, gravel
19
19
0.5
0.20
0.0
0.00
0.0
0.00
sand, pea gravel, gravel
20
20
0.0
0.00
0.0
0.00
0.0
0.00
12" sand over gravel, shell
21
n
0.0
0.00
0.0
0.00
0.0
0.00
6" mud, sand over clay
22
n
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
23
20
0.0
0.00
0.0
0.00
0.0
0.00
sand
24
26
0.0
O.OO
0.0
0.00
0.0
0.00
6" mud, sand over clay
25
49
0.0
0.00
0.0
0.00
0.0
0.00
mud
26
3
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
27
13
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand .
Samish Bay
1
47
—
—
«««•
mud
Padllla Say
1
17
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
4 QAA Qa*
2
17
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
y. accs * iy
3
23
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
ure J-2)
4
9
0.0
0.00
0.0
0.00
0.0
0.00
mud, sand
¦
S
19
0.0
0.00
0.0
0.00
I
0.0
0.00
nud, sand
-442 -
-------
I
it*
UJ
I
Reservation
MALEv (y
Ss'sJfcr ¦»
Island*
•Y-Eliia Island
SCALE IN YARDS
0 1000 2000 3000 4000 5000
Figure J-l SHELLFISH BEDS IN HALE PASSAGE
AND BELLINGHAM BAY
Source: Goodwin & Shaul 1978
-------
SAMISM BAY
60' coninur
SINCLAIR
•TTsTAfiB
Cypress Island
GUEMES ISLAMO
SCALE III YARDS 1.
o moo 3000 iboo bfino
Figure J-2 SHELLFISH BEDS NEAR SINCLAIR ISLAND,
GUEMES ISLAND, SAMISH BAY AND PADILLA BAY
Source: Goodwin & Shaul 1978
-------
APPENDIX K
BEACH TRANSECTS: PROFILES
-445-
-------
Figure K-l
beach transects; PROFILES
Source: Webber 1977
Site Number 1
Larrabee Stato Park
Rocky Bench
3-foot.
dinmeter
boulders
rock| 8 feet
high
Rocks covered with
attached Ulva and Fticus;
Mytilua eihilis , Hal anus carlonus
and B. frlandulo; numerous tidepools.
sandstone
fnce
Summary:
Sandstone cliffs drop abruptly into large rocks
below hifch tide line; rocks continue down-slope
15 meters until interrupted by very large boulder{
remainder of beach below this boulder componed of
homoftenious sandstone bedrock.
Species list (partial):
Ptorosiphonta sp.
Potrocellis sp.
sp.
Knt'iromornha
UIvm sp.
Fucus sp.
En'locladia
algae
muricata
My til no e.lulia
Mo to.icmcM scutum
Acikq-i wi tivr
1 ittorin'i sp.
HoTii rrnnnns sp.
I'fifjiiruu up.
¦molluscs
crabs
barnacles
O.rchentifl cp.
It'll.-inun r.'trionus
P'tlfnus rl'tndula
Anthoplourv xnnthof^rnwmicn
rcptintorioo hoxnetis
Pir.nf.tor cp.
water line
10
—i—
15
20
—i—
25
30
35
to
METERS DOWN BEACH
-------
sand,
^ shell fragments
Figure k-2
BEACH TRANSECTS* PROFILES
Source: Webber 1977
Site -Number 2
"Teddy Pear Cove"
Rocky Beech
cobbles
rock substrate
attached Ulvn sp. and
Fucun dintichua on rocksQ
0
and boulders.
(partial)
Specleo list;
Pnt:uru3 ep.
Ilan*i^r.">pau3 nudus
Cancor productus
Fnconi spp.
Crnnrostrea
liytilUs cdulis
l.ihtnri' n si fckana
Tlvi; hnellosn
Bnl.inuB (Qondula
llnoi'chla pnKctonsla
l«opoiis
Polychaetes
Nemerteana
Pisnoter spp*
Fucti.n distichus
Ulvn Bp.
Rii^arttno op.
Zo.'itera op.
covered
with
boulders,
cobbles,
and sand
Water line
Summary;
Sandy 'substrate containing many shells extends from
hich tide line to ei/;ht meters down-slope, then becomes
Interspersed with cobbles, bricks, gla?st etc. Rocks and
boulders dominato surface from about twenty meters to
water line.
30
—i—
15
20
7r
—I
30
35
METERS DOWN BEACH
-------
~1
o
-1
-2
«and,.
nixed shel).
fragments
5 *3
nl
§ +2 H
Figure K*3
BEACH TRANSECTS* PROFILES
Source s Webber 1977
Site Murnbor 3
"Toddy Bear Cove"
Sandy Uonch
'(partial).v
Speciea list:'
Macoma sp."
Littoring sitkana
Hytilus edulia
Saxidomus rinnnteus
Acmon digitalis
Crassostren gigas
Thnin lanollora
Clinocnrdlum nuttallii
Protothaca ptaminea
Pseudocythina rupifera
licrairrnn-u.-; nudus
Rnlfnun rrlanduln
Cancer preductus
i'nrurus spp.
Upbrohia pu^cttensia
Isopods
Ncnerteuns
llcsneronae conplanata
Pisnater ochraceua
Summary:
brickst cobbles|
sand substrate
^ rt> _ • .
Balanus
•
—i—
30
35
*K)
METERS DOWN BEACH
-------
*9
48
*7
46
+5 1
4V
g +3
s d
T. 3-
H
f- +i
Figure K-4
BEACH transects; profiles
Source: Webber 1977
Site Number 5
forth Beach
Gravel/sand Beach
O
-1
~a
pebbles,
coarse sand
substrate
fine sand
(partial)
Species lists
Thomcophelia mucronata
Kncorna bnlthica
Ox* arena r i.i
ripples
pebbles,
i I broken shells,
driftwood
Summary; Relatively homogenous gravel at highest tide levels
descends into scattered pebbles on a coarse aand
substrate. Finer, rippled sand dominates the mid-tide
level (Thoracophelia found here), interrupted l»reifly
by a band of pebbles and detritus, and then continuing
unbroken to water line.
rippled
fine sand
water line
:V.-v-.vjV--'- * ( 50 me t era )
-3
10
—I—
15
20
¦¦ r
25^
—1—
30
1 I
35
to
METERS DOWN BEACH
-------
9
*8
~7
46
~5
$ *
E *3
¦ d
s£ *2
^ ~!
- O
-1
boulders,
75cm diameter
sand
substrate
• gravel
^ *
t \ Nil • «
(partial).
Species lists
Figure K-5
BEACH TRANSECTS* PROFILES
Source s, Webber 1977
Site Number 6
North Beach
Gravel Beach
substrate
Hytilus ertulia
Dalanus carlosus
13* glanduln
Tellina sp.
ltcmicra nsis nudus
II. orr>:onenfiis
Neplitys call forniensis
Nereis vexillosa
Isopods
Arophipods
• • V£l
cobbles
nixed gravel'
*r"'*.VV"5vv and cobbles
' ' •'r-Sa.-
gravel
Summary: Large boulders on a sand substrate grade lrito 13cm cobbles on
a gravel substrate* At about 17 metersi gravel becomes the
dominant surface feature, mixed with some cobbles, and continues
to the *watcr line*
substrate
water
--^fe-Tine
-2
-3
V>
—i—
15
20
22k
i'
30
35
ko
HITTERS DOWN BEACH
-------
9 i:;i
48
~7
46
~5
4<»
-1
-2
-3
6" cobbles,
sand substrate
Figure K-6
BEACH TRANSECTS* PROFILES
Source: Webber 1977
Site Number
Pont Point
Cobble/s^nd Beach
.M *2
5 § ~*
I W
n
(partial)
Species listt
¦Zostera marina
fenestrate
Ijrrinarig
Entercmorpha inteotinalis
Cdonthalia floccosa
Henriraster exccntricus
1'isaster ochmceus
Arthonleura xanthorrrarnica
Crchcstin sp.
Amnithoe sp.
Halanus cartosus
II. ;>1 andula
Calliun/itma sp*
PaiMirus cpp.
lleraiKrapsua nudus
Clinocardium nuttallil
Thaia lamcllosa
Kytiluo cduiis
Collisella digitalis
Hotoacxoa scutum
Protothnca staminea
Kya arennHa
10
pebbles,
shell
fragments
logs.
pebbles
boulders, sand substrate,
,—V ;—-v ^ waicra
:—
1 <7/'' * ¦ t:;
Zostera
Ulva
Littorina scutulata
L. Itkana
Acmea mitra
Mncoma sp.'
Saxidomiis ftijyinteus
Antsodorus nobilis
Anthonloura xanthoflranmica
Hot'cis sp.
Giveera sp.
bVphtvs sp.
C»;roWrotulus sp.
P*>'.•onemertes sp.
r-rr^.Biatom film on
surface
homo^enious sand '
to water line (60M)
Summary; Highest tide levels consist of six
inch cobbles on a snnd/Vrnvel substrate.
Particle size decreases toward water
line, until the beach is composed of
relatively, pure sand with scattered
superficial boulders front 25 meters
to water line. Seasonally thick eel-
grass beds arc present at extreme low
tide level, with thick Dendraster
(s„nd dollar) beds scattered in sand.
—1—
15
20
Z5>
30
35
**0
METERS DOWN BEACH
-------
APPENDIX L
SAMPLING TRANSECTS AND LOCATIONS
-452-
-------
0 1000 2000
4000
500 1500 3000 yards
Nwtoack Rfcar
Lummt
Indian
Reservation
Portage
Lurrnni tel.
Point
Frances
Bellingham
Bay
Bellinghamj^pz^.
Post
Point
Chuckanut
Bay
Pleasant
Governors My
Point
Figure L-l BEAM-TRAWL SAMPLING TRANSECTS IN BELLINGHAM BAY,
MAY 1964
Source: USD! 1967
-453-
-------
JJlIJliuG jUD#
hit ¦¦
JcJ'Ji.iLiL "
Bel ling ham
{Georgia-Pacific
Corp.
/}"w /JV'v/ .
LEGEND
Rtftfrop sonpfcno
nautical miles
Figure L-2 FISHTRAP SAMPLING TRANSECTS IN BELLINGHAM HARBOR,
APRIL - JUNE 1964
Source: USDI 1967
-454-
-------
-Legend-
Tow Net
• Beach Seine
* Fyke Net
4000
500 1500 3000 yards
Noofcsack Wvar
Belliftgfeam
Lutmrri
Indian
Reservation
Bellingham
Bay
12 133
Portage
-------
Beilingham
South
Beilingham
Beilingham Bay
V//A 2
IS1 3
4
tiiSi&J shallow areas
Noullcot Miles
Figure L-4 TOWNET SECTIONS IN BELLINGHAM BAY, APRIL 27
JUl" 20, 1967
Source: Sjolseth et al. 1970
-456-
-------
Noakaaefc mvac
Strait of
Georgia
Luirnni ®ay ( / (.omnU
IMfiart
VMiOK
8attfooham
rt. Frances
Chuekanut Bay
inatt Bay P1#aMnt Ml
06
C^N
/
/jVEIiza 1st
Sinclair
lal.
San Juan
Islands
Samish Bay
Fish Pt.
Lagend
Trawl Nat
• Saach Saina
Padilla Bay
100 200
150 300
thousands of fa«t
Figure L-5. SAMPLING LOCATIONS IN BELLINGHAM BAY, APRIL 1974 -
March 1975
Source: Webber 1975
-457-
-------
Mt. Baker
Plywood
Squaffeum,
Squat teum
Creak
Bafflnghara
6>v 2
^ IAJ Waterway
,8
Bellingham
Bay
Inner
A®
'Georgis-Pacftte
Open Water
Disposal Site
(site 500 yd. west I
A
jjp •
^ Outer
M
Old Olepoaal
/
Legend-
Sampled
Frequently
9
Sampled
Occasionally
6
Boulevard
0 200 400 750 yards
100 300 500 1000
Figure L-6 TRAWLING SAMPLE LOCATION.. IN BELLINGHAM BAY,
MAY 1977 -April 1978
Source: Webber 1978
-458-
-------
APPENDIX M
STREAMBED AND FLOW CHARACTERISTICS OF THE NINE
DRAINAGES IN THE BELLINGHAM-SAMISH BASIN
-459.-
-------
APPENDIX M STREAMBED AND PLOW CHARACTERISTICS OF THE NINE
DRAINAGES IN THE BELLINGHAM - SAMISH BASIN
The 40 mile mainstem of the Nooksack River diverges into three
principal forks: South, Middle and North. (See Figure VI-16
in the main text;) The South Fork converges with the mainstem at
River Mile (RM) 36. Five more miles upstream the main Nooksack
River flows north dividing into the Middle and North Forks of
the Nooksack River. Their upper reaches range from pools and
riffles to rapids and cascading falls. Stream bottoms mainly con-
sist of gravel and rubble except for the headwaters where large
rock and boulders predominate. The lower 6-8 miles of each fork
and the mainstem of the Nooksack provides an excellent pool-
riffle stream (South Fork), broad riffles, channel splitting and
braiding (North and Middle Forks) (Williams 1975).
Squalicum Creek enters Bellingham Bay on the east side of the
city of Bellingham (Figure VI-16) . The tributary maintains a
good pool-riffle environment consisting of a gravel and rubble
stream bottom (Williams 1975).
Both Whatcom and Padd&i Creeks originate in lakes and flow through
the industrial areas of Bellingham before entering the Bay. The
lower reaches have moderate to fast riffles with dispersed pools.
The bottom is a mixture of rubble and gravel (Williams 1975).
Chuckanut Creek enters the northern portion of Chuckanut Bay
approximately .7 miles south of Bellingham. The streambed sub-
strate consists of gravel mixed with areas of rubble (Williams
1975) .
Oyster Creek flows to the northern portion of Saznish Bay (Figure
VI-16). The upper 4 miles of the creek meanders through swamps
and lakes eventually traversing steep terrain. The lower .3 miles
is a riffle stream with a gravel rubble bottom (Williams 1975).
Colony Creek enters Samish Bay .5 miles southeast of Windy Point.
Stream characterization ranges from beaver dams and debris jams
in the upper 2 miles through a steep gradient for the 'next mile
-460
-------
and finally entering a gentle gradient in the lower 2 mile reach.
This lower reach has riffles with few pools. Gravel, the pre-
dominant component of the streambed bottom is mixed with various
amounts of sand and silt (Williams 1975).
Edison Slough, the old North Fork Samish River, was formed when
dikes on the Samish River were employed for flood control (Williams
1975) .
The mainstem of the Samish River originates in a broad and flat
valley floor 29 miles upstream from its entry into the southern
area of Samish Bay (Figure VI-16). The upper reach (from RM22 -
RM29) is slow moving with marsh areas in some areas. The bottom
is composed of sand and gravel. The next 10 miles has riffles,
pools, and gravel-rubble streambeds with sandy bottom pools. The
remaining 12 miles of the lower reach is slow moving with a deep
stream course. The bottom consists of sand and silt. For flood
control purposes, dikes are located along the entire 12 mile
expanse of the lower river (Williams 1975).
-461-
-------
APPENDIX N
ANADROMOUS FISH ESCAPEMENTS AND CATCH RETURNS
-462-
-------
Table H-l NATURAL ESCAPMENTS*FOR THE BELLINGHAM - SAMISH BASIN
Source: Ames 1979, Zillgis 1979, Orrell 1979, Geist 1979, Phinney 1977
Bellingham-Samish
Be11ingham-Samish
Year
Nooksack River
Basin
Basin
Nooksack River
Samish Basin
Pinks
Chum
Coho
Chinook
Chinook
(summer-fall)
(Summer-fall)
1959
30,000
1961
100,000
1963
150,000
1965
12,500
12,740
2,600
800
1966
7,280
4,100
1,300
1967
20,000
6,370
2,800
900
1968
38,100
1,365
2,700
844
1969
15,000
25,500
2,730
1,600
500
1970
34,000
7,280
3,200
1,000
1971
40,000
7,200
4,550
4,600
1,400
1972
16,300
2,730
3,000
800
1973
75,000
39,300
4,550
3,500
1,200
1974
27,300
7,280
2,000
1,200
1975
36,000
19,000
4,550
3,030
950
1976
27,500
3,640
2,200
1,500
1977
25,000
49,300
6,370
1978
36,600
2,730
Average /year 50,350
29,100
5,297.5
2,944.2
1,032.8
*
Escapments include adults and jacks.
-------
1965
1966
1967
1968
1969
1970
1971
1972
1973
1974
1975
1976
1977
1978
Chum
16
1028
3200
120
1078
302
190
148
158
0
0
0
520
ARTIFICIAL ESCAPMENTS FOR THE NOOKSACK AND SAMISH HATCHERIES
Source: Rasch and Foster 1978
Nooksack Hatchery Samish Hatchery
Fall Chinook Coho Chum Fall Chinook Coho
0
2630
0
6228
5961
946
2459
0
2945
3698
1217
753
0
2111
6692
1185
1504
0
4312
15,917
716
2523
0
3675
15,494
1660
6898
0
2441
20,345
1930
4045
0
2711
20,137
1549
2959
0
1222
10,483
807
1823
0
2287
9200
1493
9013
0
4405
7980
1017
1602
0
2629
6575
2075
5310
0
5778
80,455
1216.3 3459.9 0 3395 16,911
-------
Table n-3 STEELHEAD CATCH RETURNS FOR THE BELLINGHAM - SAMISH BASIN
Source: Washington Department of Game 1962 - 1977
Total
Summer -
Run Catch
Total Winter - Run
Catch
Chuckanut
Nooksack
Samish
Squalicum
Chuckanut
Nooksack
Samish
Squalicum
Year
Creek
River
River
Creek
Year
Creek
River
River
Creek
1962
N/S
22
0
N/S
1961-1962
N/S
1254.6
2096
N/S
1963
N/S
7
0
N/S
1962-1963
N/S
1269
2234
N/S
1964
N/S
13
7
N/S
1963-1964
N/S
1349
2123
N/S
1965
0
23
7
0
1964-1965
2
1486
1578
14
1966
0
37
0
0
1965-1966
10
1485
2473
42
1967
0
8
22
0
1966-1967
6
1538
3410
32
1968
0
24
23
0
1967-1968
2.4
855
2695
17
1969
N/S
31
17
0
1968-1969
N/S
1196
2615
0
1970
N/S
11
30
0
1969-1970
N/S
664
1487
0
1971
0
38
20
2
1970-1971
0
963
2841
4
1972
0
29
16
8
1971-1972
11
956
3245
20
1973
0
38
2
0
1972-1973
4
955
704
10
1974
0
97
25
0
1973-1974
0
769
658
39
1975
N/S
18
5
0
1974-1975
N/S
787
849
26
1976
N/S
49
20
N/S
1975-1976
N/S
269
181
96
1977
N/S
48
0
0
1976-1977
N/S
339
895
N/S
1978
1977-1978
N/S
584
1257
36
N/S = No Survey
-------
.• * /
Bellingham
"¦•' •A' ¦' /¦ :•
'n "*>->* i
A\
X
V/ STORAGE
E
\ K \5.5
\4.° X
v.
cf^O.6
y
/A
VA V'
Georgia-Pacific
Corp. \ /.
¦' •s'v /¦' \V/ /A*-. '/
< // y-' /a\// v/ ,
V:'.
V2
V4 naut. miles
LEGEND
A Area designation
Area boundary
3.9 Average area catch
rat* (juvenile salmon
per 10 minutes of
run)
Figure N-l FISHTRAP RESULTS OF JUVENILE SALMON IN BELLINGHAM
HARBOR
Source: USDI 1967
-466-
-------
0 1000 2000
4000
500 1500 3000 yards
Nooksack River
tunimi
Indian
Reservation
Portage
Lunwm tel.
Point
Frances
Bellingham
Bay
BeltiftgJiant
Pacffid
Post
Point
inL
ChucKanut
Bay
PlMtrnt
Governors f\ Bay
Point
Figure N-2 JUVENILE SALMON PER 10 MINUTE TOW ALONG BEAM TRAWL
TRANSECTS IN BELLINGHAM BAY
Source: USDI 1967
-467-
-------
Table N-4 TOTAL CHUM, CHINOOK AND COHO CATCH PER STANDARD TOW
IN BELLINGHAM BAY, APRIL 16 - MAY 28, 1963
•Source: Tyler 1964
Tow
Station* Chum/Tow Chinoofc/Tow Cpho/Tow
1A
4
o
1
2A
3
0
1
3A
5
1
2
4A
17
1
1
5A
5
3
4
6A
3
1
2
7A
4
2
3
8A
0
2
2
9 A
15
11
0
10A
1
1
1
11A
0
1
1
12A
6
10
4
13A
3
6
5
14 A
1
5
0
15A
3
24
2
16 A
1
3
0
17 A
2
2
2
Refer to Figure L-3
-46 8
-------
Table n-5
TOTAL CHINOOK AND COHO CATCH AND CATCH OF MARKED
CHINOOK.' AND COHO SALMON PER STANDARD TOW IN THE
TWENTY-FIVE SECTIONS OF BELLINGHAM BAY, APRIL 27-
JUNE 20, 1964.
Source: Sjolseth ejt al. 1970
Bay
Sections*
Chinook/tow
Marked
Chinook/tow
Coho/tow
Marked
Coho/tow
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
19
20
21
22
23
24
25
3.54
12.17
6.00
7.36
7.20
2.90
8.00
3.33
10.20
3.67
9.57
14.71
6.50
11.53
6.00
5.60
10.80
1.20
2.10
1.45
6.60
3.61
2.00
.15
.46
.50
.33
.18
.40
.30
.94
.33
.80
.86
.71
.40
.65
.20
.40
.85
.10
.28
.40
2.92
4.17
1.92
.75
2.28
.70
1.94
.50
3.90
.17
3.50
5.29
.50
2.88
1.00
1.93
6.80
.60
.90
.55
2.20
2.44
2.00
,31
,17
33
,18
,24
,10
.31
.17
.20
.06
.20
.13
.20
.10
.10
.06
Refer to Figure L-4.
-469-
-------
Table N-6 TOTAL CHUM, CHINOOK AND COHO CATCH PER BEACH SEINE HAUL
IN BELLINGHAM BAY, APRIL 10 - JUNE 27, 1963
Source: Tyler 1964
Station *
Chum
Coho
Fall
Chinook
Pink
Station *
Chun
Coho
Fall
Chinook
Pink
1
8.0
0
0
0
20
N/D
N/D
N/D
N/D
2
0
8.0
0
0
21
0
1.0
5.0
0
3
71.3
0
0
0
22
N/D
N/D
N/D
N/D
4
0
1.0
0
0
23
N/D
N/D
N/D
N/D
5
38.0
0
0
0
24
N/D
N/D
N/D
N/D
6
146.0
15.0
3.0
0
25
N/D
N/D
N/D
N/D
7
75.0
0
0
0
26
1.0
0
3.0
0
8
1.0
20.0
0
0
27
0
0
0
0
9
29.0
0
0
0
28
N/D
N/D
N/D
N/D
10
10.0
0
1.0
0
29
6.0
3.0
15.0
0
11
4.0
1.0
0
0
30
33.0
3.0
2.0
0
12
N/D
N/D
N/D
N/D
31
N/D
N/D
N/D
N/D
13
8.0
2.0
4.0
3.0
32
0
3.0
3.0
0
14
30.0
0
1.0
0
33
N/D
N/D
N/D
N/D
15
169.0
5.0
0
0
34
N/D
N/D
N/D
N/D
16
21.0
12.0
1.0
0
35
99.0
3.0
6.0
0
17
243.0
0
0
0
36
1.0
2.0
0
0
18
8.0
2.0
0
0
37
17.0
7.0
35.0
0
19
14.0
2.0
0
0
Refer to Figure L-3
-470-
-------
Table N-7 RESULTS OF TRAWL CATCHES IN BELLINGHAM BAY, JULY 197? - MARCH 1978 (Refer to Figure L"6). Source: Webber 1979
1
2
3
6
O
ft
4
§
ft
5
H
6
7
8
U
¦p
(ft
u
•p
irt
<0
A
*
irt
*
~
«
*
§ >*
O <0
a £
-------
Table N-8 RESULTS OF BEACH SEINE SAMPLING IN BELLINGHAM BAY, MARCH 1974
Source: Webber 1975 Refer to Figure L-5
- FEBRUARY 1975
STATION LOCATION
Common Name
Scientific Name
1
2
3
4
5
6
Cabezon
Saorpaenichthys marmoratu8
0
5
0
0
5
0
High Cockscoinb
Anoplarohus purpureaoen8
0
0
0
0
1
0
Starry flounder
Platiohthya atellatu8
52
8
173
24
17
0
Whitespotted greenling
HexagvammOs atellari
2
11
0
0
0
2
Crescent gunnel
Pholia laeta
2
8
0
0
7
0
Penpoint gunnel
Apodiohthya flavidus
10
7
0
0
0
4
Pacific herring
Clupea harengua pallasii
0
0
1
0
39
55
Tubenose poacher
Pallaaina barbarta
0
0
0
0
0
2
Spearnose poacher
Agonua emmelane
28
56
3
0
0
1
Sturgeon poacher
Agonopsia aoipenserinus
0
0
0
0
0
1
Sand lance
Ammodytea nexapterua
0
0
1
0
0
0
Spiny lumpsucker
Etumiorotremus orbia
0
1
0
0
0
1
Midshipman
Porichthya nbtatua
100
0
0
0
0
0
Pile perch
Rhaooohilua vaooa
0
0
0
0
0
18
Shiner perch
Cymatogaster aggregata
9
220
21
0
128
279
Striped perch
Embiotoca lateralia
13
2
0
0
0
2
Bay pipefish
Syngnathu8 griseolinatus
9
17
0
0
3
0
Snake prickleback
Lumpenua aagitta
34
41
0
0
0
55
Chinook salmon
Onohorhynohua taohawytsoha
4
1
16
0
2
184
Buffalo sculpin
Enophrya biaon
8
12
0
1
16
21
Great sculpin
My otocephalus polyaohtho-
oephalua
4
10
0
0
7
3
Manacled sculpin
Synohirua gilli
1
1
0
0
9
0
Padded sculpin
Artediua feneatralis
101
13
0
3
3
9
Sharpnose sculpin
Clinooottua aoutioep8
26
3
0
0
32
4
Silver-spotted sculpin
Blepaiua oirrho8U8
0
0
0
0
0
1
Staghorn sculpin
Leptooottus armatus
350
100
236
153
389
74
Tadpole sculpin
Payahrolutes paradoxus
1
0
0
0
0
0
Tidepool sculpin
Oligoaottua maouloaus
450
7
0
0
128
0
Longfin smelt
Spirinohus thaleiohthys
2
1
0
0
0
0
Surf smelt
Hypomeau8 pretioaua
15
4
23
10
3
9
Tidepole snailfish
Liparis florae
4
2
0
0
4
0
Butter sole
l8opaetta iaolepsia
2
0
0
0
0
0
Flathead sole
Hippoglo88oidea elasaodon
0
0
9
0
0
0
English sole
Parophrya vetulua
35
4
4
0
0
17
Rock sole
Lepidopaetta bilineata
2
0
0
0
0
0
Sand sole
Paettiohthy8 melanoatiou8
5
1
9
7
0
1
-------
Table N-8 Continued
Common Name
Scientific Name
1
2
3
4
5
6
Three-spined stickleback
Gaatevoateua aauleatus
2
4
6
1
18
1029
Pacific tomcod
biiovogad.ua proximu8
4
42
0
18
0
6
Cutthroat trout
Salmo alarki
0
0
2
0
0
0
Tubesnout
Aulovhynchua flavidus
2
4
0
0
0
18
-------
APPENDIX 0
MARINE BIRD SPECIES
-474-
-------
Table 0-1 . MARINE BIRDS
SPECIES IN BELLINGHAM BAY
Non-
Migratory
Migratory
COMMON NAME
SCIENTIFIC NAME
Permanent
Residence
Winter
Residence
Summer Fall/Spring
Residence Miqration **
Source
LOONS
Artie loon
Gavia artica
-
X
-
1,2,3
Common loon
Gavia immer
-
X
-
1,2,3
Red-throated loon
Gavia atellata
-
X
-
1,2,3
Yellow-billed loon
Gavia adamaii
-
X
-
GREBES
Eared grebe
Podioep8 nigvicollia
-
X
2,3
Horned grebe
Podioepa awritua
-
X
-
1,2,3
Pied-billed grebe
Podilytribua podioep8
X
-
-
1
Red-necked grebe
Podioepa griaegerva
-
X
-
1,2,3
Western grebe
Aechmophorous oooidentalia
-
X
-
1,2,3
CORMORANTS
Brandt's cormorant
Phalaovocorax penicillatus *
X
X
-
1,2,3
Double-crested cormorant
Phalaavooovax auritua
X
-
-
1,2,3
Pelagic cormorant
Phalaeroaorax pelagians*
X
X
-
1,2,3
HERONS
Great Blue Heron
Ardea herodiaa
X
-
-
1,2,3
DUCKS AND GEESE
Black brandt
Branta nigricans
-
X
-
1,2,3
Bufflehead"
Bucephala albeola
-
X
-
1,2,3
Harlequin duck
Hiatvionious hi8trioncu8*
X
X
-
1,2,3
Ruddy duck
Oxyura jamaicenaia
-
X
-
1
Canvasback
Aythya valieinevia
"
X
1,2
-------
Table 0~1' Page 2
Non-
Migratory
Migratory
COMMON NAME
SCIENTIFIC NAME
Permanent
Residence
Winter
Residence
Summer Fall/Spring
Residence Miqration
Source
DUCKS AND GEESE (Continued)
Gadwall
Anua atrepera
-
X
-
1
Barrow's goldeneye
Buoephala ielandioa
-
X
-
1,2,3
Common goldeneye
Buaephala olangula
-
X
-
1,2,3
Western Canada goose
Branata o. oocidentalia
-
X
. _
1,2,3
Mallard
Anas platyrhynohoa*
X
X
-
1,2,3
Common merganser
Mergua merganser
-
X
-
1,2,3
Hooded merganser
Lophoaytee auaultatue
-
X
1
Red-breasted merganser
Mergua aerrator
-
X
-
1,2,3
Oldsquaw
Clangula hyemalis
-
X
-
1,2,3
Pintail
Anaa acuta
-
X
-
1,2
Redhead
Ay thy a amerieana
-
X
-
1
Greater scaup
Aytha mavila
-
X
-
1,2,3
Lesser scaup
Aythya affinia
-
X
-
1,2,3
Black scoter
Melanitta nigra
-
X
-
1,2,3
Surf scoter
Melanitta perapicillata
-
X
-
1,2,3
White-winged scoter
Melanitta deglandi
-
X
-
1,2,3
Northern shoveler
Anaa olypeata
-
X
-
1,2
Whistling swan
Olov oolunbidnm
-
X
-
1,3
Blue-winged teal
Anaa diaoora
-
-
X
1
Cinnamon teal
Anaa cyanoptera
-
-
X
1
Green-winged teal
Anaa oarolinenaia
X
X
-
1,2
American widgeon
Anas ameriaana
_
-
1,2,3
European widgeon
Mareoa penelope
X
~ ' ~
1
-------
Table 0-1 , Page 3
Non-
Migratory
Migratory
COMMON NAME
SCIENTIFIC NAME
Permanent
Residence
Winter
Residence
Summer Fall/Spring
Residence Migration
Source
EAGLES, HAWKS AND FALCONS
Northern Bald eagle
Haliaeetue leuaooephalua*
X
X
-
1,2,3
Peregrine £alcon
Falco peregrinua
-
X
-
1
Osprey
Pcmdion haliaetua
-
-
X
2
Pigeon hawk
Faloo aolumbariue
-
X
-
1
CRANE
Sandhill crane
Gvub canadensis
-
-
X
1
RAILS
American Coot
Fulica americana
-
X
-
1,2
PLOVERS
Killdeer
Charadriua vooiferus
X
--
-
1,2,3
American Golden plover
Pluvialis dominiaa
-
¦-
X
1
Black-bellied plover
Squatavola squatarola
-
-
X
1
Semi-palmated plover
Charadr>iu8 8emipalmatu8
-
-
X
1
SANDPIPERS AND OTHER SHOREBIRDS
Short-billed dowitcher
Limnodromus griaeua
-
-
X
1,2,3
Dunlin
Ertolia alpina
-
X
-
1,2,3
Sanderling
Croaethia alba
-
X
-
1,2,3
Least sandpiper
Erolia minutilla
¦-
-
X
1,2,3
Pectoral sandpiper
Evolia melcmotoa
-
-
X
1,2,3
Rock Sandpiper
-
X
-
1
Spotted sandpiper
Aotitia manoulari-a
-
-
X
1,2,3
Western sandpiper
Eveunetea mauri
X
1,2,3
-------
Table 0-1 , page 4
Non-
Migratory
Migratory
COMMON NAME
SCIENTIFIC NAME
Permanent
Winter
Summer Fall/Spring
Source
Residence
Residence
Residence. Migration
SANDPIPERS AND OTHER
SHOREBIRDS, Continued
Common snipe
Capella gallinago
-
¦ -
X
1
Surfbird
Aphriza virgata
-
X
-
1,2,3
Black turnstone
Arenavia melanoaephala
- ¦
X
-
1,2,3
Ruddy turnstone
Arenaria interpves
-
-
X
1,2,3
Whimbrel
Nimeniua phaeopus
-
X
1,2,3
Greater yellowlegs
To tonus melanoleuous
-
-
X
1,2,3
Lesser yellowlegs
Totanua flavipea
-
-
X
1.3
PHALAROPES
Northern phalarope
Lobipes lobatus
-
-
X
1,2,3
JAEGERS
Parasitic jaeger
Stercorariua parasiticus
-
-
X
1,2,3
GULLS AND TERNS
Bonaparte's gull
Larua Philadelphia
-
-
X
1,2,3
California gull
Lama californioua
-
-
x
1,2,3
Franklin's gull
Lotus pipixcan
-
-
*
1
Glacous gull
Larua hypevboveue
-
X
-
1
Glacous-winged gull
Larua glauceaoena*
X
X
-
1,2,3
Heermann's gull
Lams heermanni
-
-
x
1,2,3
Herring gull
Larue argentatus
-
X
-
1,2,3
Mew gull
Larus camia
-
X
-
1,2,3
Ring-billed gull
Lamia delauarenais
-
-
- X
1,2,3
Thayer's gull
Lotus thaveri
-
X
- .
1,2,3
Western gull
Larua occidentalia
X
— —
1,2,3
-------
Table P-l , P^ge 5
Non-
Migratory
Migratory
COMMON NAME
SCIENTIFIC NAME
Permanent
Winter
Summer Fall/Spring
Source
Residence
Residence
Residence Migration
GULLS AND TERNS, Continued
Black-legged Kittiwake
Risaa tridactyla
-
-
X
i
Common tern
Sterna hirundo
-
-
X
1,2,3
ALCIDS
Rhinoscerus auklet
Cevorhinoa monooerata
-
-
2,3
Pigeon guellemot
Ceepphua columba*
X
X
1,2,3
Common murre
Uria aalge
-
X
-
1,2,3
Marbled murrelet
BraohyramphuB marmoratus*
X
X
-
2,3
Tufted puffin
Lunda oirrhata
-
x
2,3
KINGFISHERS
Belted kingfisher
Megaoeryle aloyon
X
1,2,3
* Some individuals of the species are permanent residents in the study, area. Due to the fall migrating, winter
resident individuals of this species, populations are greatest at this time.
Source Key: 1. Webber 1975
2. Salo 1975
3. MSN 1977
*
Represe»._s bird species that utilize Bellingham Bay to rest or feed during migratory flights. This does not
include migratory species that remain in the area as seasonal residents.
-------
APPENDIX P
BIRD CENSUS METHODS
-480-
-------
CENSUS METHODS
Point Census
Sea Watch
Beach Census
Beach Walk (Dead
Bird Census)
Small Boat Census
Ferry Census
Aircraft Census
-481-
A periodic census taken from a shore location.
All birds flying or on the water visible with
binoculars or a telescope were counted.
Using a telescope in most cases, all birds
moving past a fixed designated point were
recorded. Observations were made from dawn
for 2-3 hours and 2-3 hours previous to
dark.
Count of all birds along a defined distance
of beach from high tide to approximately
100 meters offshore.
Count of all dead birds along a designated
distance of beach from the water's edge
to upper tidal level.
Periodic in-motion boat census of birds
occurring in open waters, shorelines, small
islands and rocks.
Experienced observers aboard ferries made
monthly counts of birds in open waters,
passages, and along shorelines. The ferries
boarded included: Port Townsend - Keystone;
Port Angeles - Victoria, B.C.; Anacortes -
Sidney, B.C.; and Tsawwassen - Swartz Bay,
B.C.
Monthly census of birds was made from a
small aircraft flying 60 meters above the
water's surface. The unaided eye was used
to make the counts.
-------
APPENDIX Q
SEASONAL PROJECTIONS OF BIRD DENSITY AND NUMBERS
-482-
-------
Table Q-la SEASONAL PROJECTIONS OF BIRD DENSITY AND NUMBERS FOR
SAMISH Bay
Source: Manuwal et al. 1979
Period
Family
Area
Spring
Summer
Fall
Winter
Loons
S
D=
1.67
0.08
0.71
0.97
PT=
50
2
20
30
w
D=
7.65
1.43
4.12
13.41
PT=
270
50
150
500
Sums
PT=
320
50
170
530
Grebes
s
D=
56.25
-
36.85
67.67
PT=
1,600
—
1,100
2,000
w.
D=
122.16
-
202.75
65.45
PT=
4,300
—
7,200
2,400
Sums
PT»
5,900
-
8,300
4,400
Cormorants
S
D=
1.00
0.31
1.89
1.36
PT=
30
9
60
40
W
D=
0.39
-
2.94
0.68
PT=
10
—
100
30
Sums
PT=
40
9
160
70
Herons
S
D=
2.03
7.29
3.41
0.60
PT=
60
210
100
20
W
D=
0.39
-
-
PT=
10
—
—
-
Sums
PT»
70
210
100 .
20
Ducks and
S
D=
401.84
1.35
243.85
332.75
Geese
PT=
1,200
40
7", 300
9,600
W
D=
459.61
14.29
59.61
1,123.18
PT=
16,000
500
2,100
42,000
Sums
PT=
17,000
540
9,400
52,000
Eagles and
S
D=
0.05
Hawks
PT=
-
-
-
1
w
P"
—
¦ _
0.681
PT=
-
-
-
1
Sums
PT=
-
-
-
2
Rails
S
D=
0.02
_
0.02
PT=
<1
-
-
1
Plovers
S
D=
4.63
0.48
2.97
1.18
PT=
130
14
90
30
Continued
-483-
-------
Table Q-la Continued
Period
Family
Area
Spring
Summer
Fall
Winter
Sandpipers and
S
0=
233.02
¦ 112.73
53.38
83.63
other shores
PT=
6,800.
3,300
1,100
2,400
birds
Gulls and
S
D=
40.08
10.69
35.38
7.36
Terns
PT=
1,200
310
1,100
210
W
D=
24.51
2.14
8.63
87.27
PT®
870
80
300
3,200
Sums
PT»
2,100
390
1,400
3,400
Alcids
S
0.06
0.40
0.35
0.12
PT=
2
10
10
3
W
D=
0.78
1.43
1.18
20.91
PT=
30
50
40
770
Sums
PT="
30
60
50
770
Summary
S
D=
379.31
134.48
379.31
48.28
PT=
11,000
3,900
11,000
14,000
w
D-
677.42
21.94
319.35
1,580.65
PT»
21,000
680
9,900
49,000
Sums
PT»
33,000
4,600
21,000
63,000
1. Numbers adjusted to allow for small sample size.
Key:
D = Calculated Density (BirdsA®2)
PT = Projected Totals
Sums = Summary
H = Open Hater Habitat
S = Shoreline Habitat
- - no observations of the appropriate species
-484-
-------
Table Q-lb SEASONAL PROJECTIONS OF DENSITY AND NUMBERS FOR
BELLINGHAM BAY
Source: Manuwal et al. 1979
Period
Family
Area
Spring
Summer
Fall
Winter
Loons
S
D=
0.81
0.15
0.08
1.26
PT=
30
6
3
50
W
D=
3.70
-
3.96
6.24
PT=
450
—
490
760
Sums
PT=
480
6
490
810
Grebes
S
D=
17.99
4.94
45.61
114.44
PT=
650
200
1,600
4,100
W
D=
43.84
3.33
67.03
147.23
PT=
5,300
410
8,200
18,000
Sums
PT=
6,000
610
9,800
22,000
Cormorants
S
D=
2.13
0.46
3.07
5.38
PT=
80
20
110
190
W
D=
1.64
0.21
0.54
5.82
PT=
200
30
70
710
Sums
PT=
280
50
180
900
Herons
D=
0.70
1.64
0.80
0.42
PT=
30
60
30
20
Ducks and Geese
S
D=
33.50
3.11
14.73
67.74
PT=
1,300
110
530
2,400
W
D=
3.97
-
-
37.52
PT=
490
•
4,600
Sums
PT=
1,800
110
530
7,000
Eagles and Hawks S
D=
0.23
0.06
0.07
0.20
PT=
8
2
3
7
Rails
S
D=
0.02
-
0.01
0.08
PT=
1
<1
3
Oystercatchers
S
D=
-
-
0.02
-
PT=
•
1
•
Plovers
S
D=
0.07
0.19
0.07
0.04
PT=
3
7
3
1
Sandpipers and
s
D=
10.77
0.27
11.91
8.63
other shorebirds
PT=
390
10
430
310
Jaegers
S
D=
-
-
0.01
-
PT=
•
•
<1
*
Continued
-485-
-------
Table Q-lb Continued
Period
Family Area
Spring
Summer
Fall
Winter
Gulls and Terns S
D=
26.95
21.91
36.44
24.21
PT=
970
790
1,300
870
W
D=
13.90
4.79
23.60
34.82
PT=
1,700
580
2,900
4,200
Sums
PT=
2,700
1,400
4,200
5,100
Aleids S
D=
0.71
1.20
0.75
1.12
PT=
30
40
30
40
W
. D=
0.21
0.83
50.09
33.83
PT=
25
100
6,100
4,100
Sums
PT=
50
140
6,100
4,100
Summary S
Da
97.22
33.33
111.11
222.22
PT=
3,500
1,200
4,000
8,000
W
D-
67.21
9.01639
147.54
26.23
PT=
8,200
1,100
18,000
32,000
Sums
PT=
12,000
2,300
22,000
40,000
Key:
D = Calculated Density (Birds/km2)
PT = Projected Totals
Sums = Summary
W » Open water habitat
S « Shoreline habitat
- = no observations of the appropriate species
-486-
-------
Table Q-lc SEASONAL PROJECTIONS OF DENSITY AND NUMBERS
HALE PASSAGE
Source: Manuwal et al. 1979
FOR
Family
Area
Spring
Period
Summer
Fall
Winter
Loons
D=
PT=
2.94
50
0,50
8
0.35
6
5.14
80
Grebes
D=
PT=
5.21
80
4.43
70 .
17.68
280
Cormorants
D=
PT=
1.03
20
0.10
2
0.39
6
1.38
20
Herons
D=
PT=
0.03
<1
0.95
20
0.08
1
0.03
<1
Ducks and
Geese
D=
PT=
18.95
300
0.85
10
1.33
20
31.76
510
Eagles and
Hawks
D=
PT=
0.03
<1
0.04
1
0.11
2
Sandpipers and
other
shorebirds
D=
PT=
6.08
100
Jaegers
D=
PT=
0.03
<1
Gulls and
Terns
D=
PT»
96.38
1,600
17.75
290
15.65
250
10.86
170
Alcids
D*
PT=s
1.44
20
3.55
60
2.35
40
4.46
70
Summary
D=
PT=
126.18
2,000
23.70
380
24.63
400
77.51
1,20Q
Key:
D = Calculated Density (Birds/km^)
PT = Projected Total
Sums = Summary
W = Open Water habitat
S = Shoreline habitat
- = no observations of the appropriate species
t4 87-
-------
APPENDIX R
GEOGRAPHICAL HABITAT TYPES USED BY BIRD SPECIES
488-
-------
KEY TO GEOGRAPHICAL HABITATS FOR TABLES VI-21 and R-l
Source? MSN 1977
Ocean Waters - From beach to 3.0 miles off shore. Includes all types of
bottom configurations and types. Ocean coast. See next category.
Major Entrance Channels - Channels where currents and food resources are
conspicuously concentrated: Columbia River mouth, entrances to Willapa
Bay and Grays Harbor, Admiralty Inlet, and Deception Pass where all
southern waters connect with Strait of Juan de Fuca.
Sandy Ocean Beach - Land area only, of sand and/or mixed fine.
Rocky Ocean Beach - Land area only, predominately of large rocks and/or
mixed coarse.
Channels. Submerged Reefs - Water areas in protected or "inside" waters,
significant for feeding concentrations. (Large open straits often do
not show as much biological activity as adjoining channels between
islands, etc.)
Rocky Islands - Land areas both off the ocean coast and inside waters,
including those covered with top-soil and vegetation (Destruction and
Protection Islands, etc.)
Sandy Islands - Land areas, including gravel and sand types, in Willapa
Bay, Grays Harbor, Puget Sound.
Tidal Flats - Both unexposed and exposed stages - not an Immediate part
of an estuary itself but including flats below beaches as on inside of
Long Beach Peninsula, etc.
Small Estuary - Mouths of small streams in "inside waters" with no
significant salt marsh or streams emptying directly into the ocean on
the coast behind accreted spits, etc. Includes both land and water
areas. Rated low individually, but important as a category in total.
Large Estuary - River delta with salt marsh and sloughs, but for pur-
poses here not including large estuarine systems like Willapa Bay and
Cray* Harbor. I.arvJ an'l wattr areas.
Salt Marsh - Large, not in immediate estuary itself, and including only
land area of marsh itself. (As at Ledbetter Point, adjoins tidal flats.
Because of extent, provides significant habitat for specialized birds,
like Pectoral and Least Sandpipers).
Sandy Spit - Accreted land area of sand and/or gravel adjunct to large
island or mainland.
Jetty - Land area only of rock breakwaters and groins. Man-made habitat
now very significant for several species of birds in Washington (and
likely also for feeding fish and marine mammals). Substitute rocks, but
probably better because of location at important channels.
Sandy Beach - Land area only of undeveloped sand/gravel shore in protected
waters.
Rocky Beach - Land area only of rocky beaches in protected waters.
Protected Waters - Small harbors, etc., in Puget Sound, often in developed
-------
Table R-l GEOGRAPHICAL habitat types used by species* occurring ih BELLINGHAM AMD samish bays
Channels,
Major Submerged Undeveloped Protected
Ocean Entrance Ocean Beachea Reefa, Islands Tidal Estuariea Salt Sandy Ocean Beaches Harbors
Waters Channels Sandy Rocky etc. Rocky Sandy Flats Small Large Marsh Spita Jetties " Sandy Rocky etc.
Comon boon
X
X
X
X
X
X
X
Arctic Loon
X
X
XX
Red-throated Loon
X
X
X
X
X
X
X
Red-necked Grebe
X
X
X
X
X
X
X
Horned Grebe
X
X
X
X
X
X
Eared Grebe
X
X
X
X
Western Grebe
X
X
X
X
X
X
Double-crested
X
XX
X
XX
X
X
X
X
X
Coraorant
Brandt's Coraorant
X
XX
X
XX
X
X
XX
X
X
Pelagic Coraorant
X
XX
XX
XX
X
X
XX
X
X
Great Blue Heron
X X
X
X X
X
X
X
X
X
X
X X
X
Whistling Swan
X
X
X
Coamon Goldeye
X
X
X
X
X
Barrow's Goldeye
X
X
XX
Bufflehead
X
X
X
XX
Oldsquaw
X
XX
X
Harlequin Duck
X
X
X
X
X
X
Nhite-winged Scoter
XX
XX
X
X
X
Surf Scoter
XX
XX
X
X
X
Black Scoter
X
X
X
X
X
Ruddy Duck
X
X
X
Hooded Merganser
X
X
X
XX
1 Coamon Merganser
^ Red-breasted
X
X
X
X
X
X
X
X
X
X
U> Merganser
O Bald Eagle
* Osprey
X X
X
X
X
X X
X
X
X
X
American Coot
X
X
X
Canadian Goose
X
X
X
X
X
X
Brant
X
X
X
X
X
X
Mallard
X
X
X
X
X
X
X
Pintail
X
X
X
X
X
Green-winged Teal
X
X
X
X
X
American'Nigeon
X
X
X
X
X
Northern Shoveler
X
X
X
Canvasback
X
X
X
Greater Scaup
X
X
X
Lesser Scaup
X
X
X
Senipalnated Plover
X
X
X
X
X
Killdeer
X
X
X
X
X
Anerican Golden
X
X
X
Plover
Black-bellied Plover
X
XX
X
X
X
X
Surfbird
X
X
XX
X
Ruddy Turnstone
X
X
X
X
X
X
Black Turnstone
X
X
X
XX
X
Common Snipe
X
X
Whinbrel
X
X
X
X
X
X
Spotted Sandpiper
X
X
X
X
Greater Yellowlegs
X
X
X
X
X
X
Lesser Yellowlegs
X
X
X
X
X
X
continued
-------
Table R-l, Pg. 2
Channels,
Major
Submerged
Undeveloped
Protected
Ocean
Entrance
Ocean
Beaches
Reefs,
Islands
Tidal
Estuaries
Salt
S Aiidy
Ocean
Beaches
Harbors
Species
Waters
Channels
Sandy
Rocky
etc.
Rocky
Sandy
Flats
Small
Larqe
Harsh
Spits
Jetties
Sandy
Rocky
etc.
Rock Sandpiper
X
XX
X
XX
X
Pectoral Sandpiper
X
X
Least Sandpiper
X
X
X
X
X
X
Dunlin
XX
XX
X
X
X
X
X
Short-billed
X
X
X
X
Dowitcher
Western Sandpiper
X
X
X
X
X
X
X
Sanderling
XX
X
X
X
XX
X
Northern Phalaxope
XX
X
X
X
X
X
X
Parasitic Jaeger
X
XX
X
X
X
X
Glaucous-winged Gull
XX
XX
XX
X
XX
XX
X
X
X
X
X'
XX
X
X
X
Western Gull
XX
XX
XX
X
X
XX
X
X
X
X
XX
X
X
Berring Gul l
XX
X
X
X
X
X
X
X
X
X
X
X
X
Thayer's Gull
X
X
XX
X
X
X
X
X
X
X
X
X
X
California Gull
XX
XX
XX
X
X
X
X
X
X
X
X
XX
X
X
X
Ring-billed Gull
X
X
X
X
X
X
X
X
X
Mew Gull
X
XX
X
X
X
X
X
X
X
X
X
X
Bonaparte'a Gull
X
X
K
XX
X
X
X
X
X
X
X
X
X
Ueernan's Gull
- X
XX
XX
K
XX
X
X
X
X
X
XX
X
X
Black-legged
XX
XX
X
X
X
X
X
X
X
XX
I Kittiwake
^Common Tern
X
X
X
X
X
X
X
X
X
X
t-j Common Hurre
XX
XX
XX
XX
X
1 Pigeon Guillemot
X
X
XX
X
X
X
Marbled Hurrelet
X
X
X
X
Rhinoceros Auk let
X
XX
XX
XX
X
Tufted Puffin
X
X
X
XX
Belted Kingfisher
%
X
X
X
X
X
X
X
Qua to insufficient data, not ill species are represented. Sourcei MSN 1977
Key i
X ¦ occurs in habitat
XX " preferred habitat type
-------
|