HISTORY, DISPERSION AND EFFECTS
     OF PULPMILL EFFLUENTS
      ON RECEIVING WATERS:
   PORT ANGELES, WASHINGTON
         FINAL REPORT j

        JANUARY, 1981

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NORTHWEST ENVIRONMENTAL CONSULTANTS, INC.
       158 Thomas Street, Suite  32
        Seattle, Washington 98109
     HISTORY, DISPERSION AND EFFECTS
          OF PULPMILL EFFLUENTS
           ON RECEIVING WATERS:
        PORT ANGELES, WASHINGTON
              FINAL REPORT

             JANUARY, 1931
By:
G. Bradford Shea - Project Director  (NEC)
Curtis C. Ebbesmeyer - Oceanography Director  (EHI)
Quentin J. Stober - Toxicity Consultant  (UW)
Kathryn Pazera (NEC)
Jeffrey M. Cox (EHI)
Jonathan M. Helseth (EHI)
Susan Hemingway (NEC)
Submitted to:
U.S. DEPARTMENT OF JUSTICE, and
U.S. ENVIRONMENTAL PROTECTION AGENCY

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ACKNOWLEDGEMENTS
This report was made possible through the continuing support
of the U.S. Department of Justice and U.S. Environmental
Protection Agency in Seattle. In addition, the cooperation
and support of numerous scientists and agency officials at
EPA’S Corvallis and Newport Laboratories, at the Washington
Departments of Ecology, Fisheries and Game and at the (Jniver-
sity of Washington provided the data with which to construct
the physical, chemical and biological dynamics of the Port
Angeles system. We also thank the EPA personnel for their
review conunents on earlier versions of this report.
The authors wish to especially acknowledge the continuous
staff support of Ms. Cynthia Clay, typing and production,
Ms. Diane Koran, Cartographer and Graphics Artist and Ms. Linda
McCoy, Office Manager at NEC. Oceanographic graphics and
photographs were produced by Terry L. Storms and David B.
Browning, respectively at EHI.
2 .

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NOTE ON UNITS AND ABBREVIATIONS
Metric units are used as the standard for this report. In
many cases, however, data on effluents, fish, or other quanti-
ties is uniformly reported in English units. In these cases,
we have usually preserved the English units and, where conven-
ient, have placed the metric equivalent in parenthesis or at
least given a conversion factor.
Abbreviations 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
referred 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.
1].

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LIST OF ABBREVIATIONS*
BOD Biochemical Oxygen Demand
COD Chemical Oxygen Demand
CZ Crown Ze].lerbach Corporation (or pulpmill)
DMR Daily Monitoring Report
DO Dissolved Oxygen
DOC Dissolved Organic Carbon
DOE Washington State Department of Ecology
EHI Evans Hamilton, Inc.
EPA U.S. Environmental Protection Agency
FHL Friday Harbor Laboratory, University of Washington
FRI Fisheries Research Institute, University of Washington
FWPCA Federal Water Pollution Control Administration
ITT ITT Rayonier, Inc. (or pulpmi].l)
ITT Rayonier Monthly Environmental Report
MSN Mathematical Sciences Northwest
NEC Northwest Environmental Consultants, Inc.
NPDES National Permit Discharge Elimination System
NOAA National Oceanographic and Atmospheric Administration
NOS National Ocean Survey
P81 Pearl—Benson Index
PCHB Pollution Control Hearings Board
pH Hydrogen Ion Concentration
PNRBC Puget Sound Task Force of the Pacific Northwest
River Basins Commission
RMP Refiner Mechanical Process
SCS Suspended Combustible Solids
iii

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SME Sulfite Mill Effluent
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
TMP Thermomechanica]. Process
TOC Total Organic Carbon
TS Total Solids
TSS Total Suspended Solids
TVS Total Volatile Solids
USCGS U.S. Coast and Geodetic Survey
USD1 U.S. Department of the Interior
USGS U.S. Geological Survey
UW University of Washington
WDF Washington State Department of Fisheries
WDG Washington State Department of Game
WPCC Washington State Water Pollution Control Commission
*Certain other specialized abbreviations (i.e., chemical sym-
bols etc.) are defined in individual chapters. Abbreviations
above are used at various points in the report.
iv

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TABLE OF CONTENTS
Page
List of Abbreviations iii
EXECUTIVESUMNARY Xvii
VOLUME I (Chapters I - V )
I. HISTORY OF PULPMILLS AT PORT ANGELES, WASHINGTON . . 1
A. Crown Zellerbach . . . . . . . . . . . . . . . . 4
B. Fibreboard . . . 27
C. ITTRayonier 29
References 69
II. INDUSTRIAL AND MUNICIPAL EFFLUENTS AND COMPOSITION 81
A. Effluent Dischargers . • • . 81
B. Mill Closures 121
C. Effluent Composition and Toxicity 123
References . . . . • 139
III. OCEANOGRAPHICDYNAMICS . 144
A. Existing Literature and Dynamics 144
B. Physical Setting . . . . . . 154
C. Dynamics . . . . . . . . . . . . . . . . . . . . 162
References . . . . . . . 165
IV. WATER QUALITY . . . . . . . . . . . 169
A. Water Quality Criteria 170
B. Water Quality Monitoring 174
C. EPA Field Studies 195
References • • . • 165
V. TOXICITY . . . . . . . .
A. Literature Review of Sulfite Mill Effluent
Toxicity . . . . . . . . . . . . 213
B. Gross Toxicity Bioassays . . . . . . . . . . . . 221
C. Receiv3.ng Water Bioassays. . . . . . . . . . . . 228
D. Major Effluent Compounds and Organism Response . 233
References . . . . . . . . . . . . 248
Volume II (Chapters VI - IX )
VI. BIOLOGICAL RESOURCES . . . 254
A. PhytoplanktOn and Other Marine Plants. . . . . . 254
B. Zooplankton. . . . . . . . . . . . . 267
C. Shellfish . 277
D. Other Marine Invertebrates . . . . 296
E . Fish . . . . . . . . . • , . , • 318
F. Wildlife . . . . . . . . . . . . . . . , . . . , 346
References . . . . . . . . . . . . . . . . • , , 366
V

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VII. ECOLOGICAL EFFECTS .
A. Primary Production.
B. Secondary Production. -
C. Damage Mechanism. .
D. Ecosystem Effects .
References. - . . .
VIII. ANALYSIS AND RESULTS
A. Oceanographic Dynamics.
B. Water Quality . . .
C. Toxicity
D. Biological and Ecological
References.
IX. CONCLUSIONS .
VOLUME III (Appendices )
Page
372
373
. . 378
• • . . . • . • . . . 384
. . . . . • . . . . . 388
• . . . . . . . . . . 391

.
.
Effects . .

499
I—A.
I—B.
I-C.
I—D.
I -E.
I-F.
I -G.
I—H.
I—I.
I —J .
I-K.
I -L.
I-M.
Chapter I:
. — . . —
• . . . —
. . . . —
• • . . .

• . . .
• . . — —
— . . . .
. • — —
• • . —
. • . • •
• U • S
. . U • S
• . A—i
• . A—4
A—8
.A—li
•A— 13
.A—16
•A—24
• .A—27
• .A—30
• .A—33
.A—35
• .A—38
• .A—4].
111-A. SUMMARY OF CURRENT 1 TER OBSERVATIONS . • .
Ill-B. OBSERVATIONS OF WATER PROPERTIES IN PORT ANGELES
AND VICINITY
Ill-C. SURFACE SSL AND SALINITY IN THE HARBOR. . .
III-D. AERIAL PHOTOGRAPHS OF PORT ANGELES HARBOR AND
VICINITY. . • . . . . . . . • . . . . • . . . .
Chapter IV: No Appendices
Chapter V:
V—A. TOXICITY TESTS, METHODS AND EFFECTS . . . . . . • .A—97
V—B. OYSTER BIOASSAY METHODS . . . . . . . . . . . . • A—106
• . 396
• 396
. . 448
. . 464
• . 482
. 494
GROUNDWOOD PULPING PROCESS.
CROWN ZELLERBACH PROCESS. . . .
CROWN ZELLERBACH SLUDGEBEDS
CROWN ZELLERBACH PRIMARY TREATMENT.
CROWN ZELLERBACH SECONDARY TREATMENT.
CROWN ZELLERBACH OVERFLOWS AND SPILLS
THE SULFITE PROCESS . . . . . .
DISSOLVING PULPS. . . .
ITT RAYONIER PRIMARY TREATMENT. . •
ITT RAYONIER SLUDGEBEDS
ITT RAYONIER SECONDARY TREATMENT.
ITT RAYONIER SSL RECOVERY . . . . .
ITT RAYONIER SPILLS AND VIOLATIONS.
Chapter II: No Appendices
Chapter III:
.A—67
.A—76
A— 81
.A—95
vi

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Chapter VI: Page
VI-A. TOTAL PHYTOPLANKTON SAMPLED FOR STATION 2 . . . . A- 115
VI-B. SALTWATER MARSH VASCULAR PLANTS FROM DUNGENESS SPITA- 118
VI-C. PERCENT RELATIVE ABUNDANCES OF DOMINANT
ICTHYOPLANKTON TAXA COLLECTED BETWEEN ANGELES
POINT AND DUNGENESS BAY A- ’ 2 °
VI-D. DISTRIBUTION OF SUBTIDAL CLAMS, CLAM SHELL
DEPOSITS, HARDSHELL CLAM TRANSECTS AND MAJOR
CLAMBEDS FROM PORT ANGELES TO DUNGENESS BAY . . . A- i 23
VI-E. LOCATION OF GEODUCK TRANSECTS AND MAJOR GEODUCK
BEDS: ANGELES POINT, GREEN POINT AND DUNGENESS
BAY . . . . . . . . . . . . . . . . . , , . . . . A—i 35
VI-F. BENTHIC INVERTEBRATES . . . . . . . A- 1 4 2
VI-G. BENTHIC, EPIBENTHIC AND PELAGIC INVERTEBRATES
SAMPLED IN LITTORAL AND SUBLITTORAL AREAS . . . . A- i 46
VI-H. LOCATIONS OF BEACH SEINES AND FISH SURVEYS
CONDUCTED IN THE STRAITS. . . A- ] - 73
VI-I. STREAMBED AND FLOW CHARACTERISTICS OF THE
TWELVE DRAINAGES IN PORT ANGELES AREA A-177
VI-.J. SALMON SPAWNING DATA . . . . . . . . . . A-181
VI-K. MARINE FISH ABUNDANCE AND BIOMASS A-189
Chapter VII:
VII—A. SEASONAL FOODWEBS AT MORSE CREEK AND DUNGENESS
SPIT. . . . . . . . . . . . . . . . . . . . . . • A — 203
Chapter VIII:
VIII-A. CALCULATION OF BULK RESIDENCE TINE FROM SSL DATA. A-216
VIII-B. LETTER TO DOE FROM PROF. CLIFFORD A. BARNES
ON DOWNWARD TRANSPORT PROCESS IN THE PUGET
SOUNDSYSTEM. . . . . .A—220
vii

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LIST OF FIGURES
Page
I—i.
Location of Port Angeles Pulpmills .
2
1—2.
Crown Ze].lerbach Discharge Locations
9
1—3.
ITT Rayonier Discharge Locations
33
1-4.
Schematic of Waste Sources (1970), ITT Rayonier .
39
1—5.
Schematic of Waste Sources (1977), ITT Rayonier .
40
1—6.
Schematic of Waste Sources (1980), ITT Rayonier .
41
11—1.
DOE Water Classifications at Port Angeles . . . .
82
11—2.
Known Discharging Facilities. .
85
11—3.
Know Outfalls Discharging to Port Angeles Harbor.
86
11-4.
Known Woodwaste Fills, Logyards and Landfills . .
88
11—5.
Port Angeles Monthly Average for Effluent Flow. .
91
11—6.
Crown Zellerbach Monthly Average - SCS
94
11-7.
Crown Zellerbach Monthly Average - TS
95
11—8.
Crown Zellerbach Monthly Average - Zinc . . . . .
97
11—9.
Crown Zellerbach Monthly Average - BOD
98
11—10.
Crown Zellerbach Monthly Average - TSS. . . . . .
100
11—11.
Fibreboard Monthly Average — SCS. . . . . . . . .
102
11—12.
Fi.breboard Monthly Average — TS . . . . . . . . .
103
11—13.
ITT Rayonier Monthly Average — SCS. . . . . • . .
105
11—14.
ITT Rayonier Monthly Average — TS . . . . . . . .
107
11—15.
ITT Rayoriier Monthly Average — BOD. .
109
11—16.
ITT Rayonier Monthly Average — TSS. . . . . . . .
111
il l—i.
Oceanographic Study Area and Approaches . . . . .
145
111-2.
Expanded View of Study Area and Approaches. . . .
111—3.
Schematic of the Hydraulic Tidal Model. . . . . .
153
111—4.
111—5.
Bathymetry Within The Study Area and Port An e1es
harbor . •
Topography Within the Study Area.
155
158
111—6.
Seasonal Cycles of Air Temperatures,
111—7.
Precipitation and Runoff. . . . . . . . . . . . .
Seasonal Progression of Prevailing Winds. . . . .
159
161
111—8.
Wind Speed and Direction. . . . . . . . . . . . .
163
IV—1.
Main STORET Sampling Stations, Port Angeles Area.
175
IV—2.
Main STORET Sampling Stations,
IV—3.
PortAngelesHarbor . . .
Surface SSL and DO. Correlations
176
183
IV-4.
SSL Concentrations at 4 Stations in
PortAngelesfiarbor
186
IV—5.
Surface SSL in Port Angeles Harbor,
November 1962 — December 1963 .
187
IV—6.
Surface SSL in Port Angeles Harbor,
August 30, 1963 . . . . . . . . . . . . . . . . .
188
IV—7.
Surface SSL in POrt Angeles Harbor,
IV—8.
September 8, 1963 . . . . . . . . . . . . . . . .
Surface SSL and D.O. Correlations, Survey #1. . .
189
191
IV—9.
Surface SSL and D.O. Correlations, Survey #2. . .
192
IV—10.
Surface SSL and D.O. Correlations, Survey #3. . .
194
viii

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Page
IV—11. Water Quality Stations of the Thunderbird. . . . 196
IV—12. Water Quality Stations of the Streeter 197
V—i. Variability Between Port Angeles and
BellinghainSSLEffects . 215
V-2. Degradation of Chlorine in Aquatic Systems . . . 239
VI—1. Strait of Juan de Fuca Station Locations . . . . 258
VI—2. Diatom Concentrations in the Strait 261
VI—3. Dinoflagellate Concentrations in the Strait. . . 262
VI—4. Macro-algae and Seagrass Beds — Port Angeles . . 264
VI—5. Icthyoplankton Stations. . . . . . . . . . . . . 271
VI—6. Zooplankton Stations . . . . . . . . . . . . . . 276
VI-7. Major Hardsheil Clam, Geoduck Clam and
PacificOysterBeds 285
VI—8. Port Angeles Harbor Intertidal Beach Samples . . 292
VI—9. Comparison of 1970 and 1975 Clam Surveys . . . . 294
VI-lO. Thickness and Distribution of Sludge Deposits —
ITTRayonier. . . . . . . . . . . . . . . . . . 309
VI—li. Distribution of Percent Volatile Solids in
Sediments — ITT Rayonier . . . . . . . . . . . . 310
VI—12. Benthic Sampling Stations and Areas of Damage. . 312
VI-j.3. Thickness and Distribution of Sludge Deposits -
Crown Zellerbach - . . . . . . 314
VI—14. Distribution of Percent Volatile Solids in
Sediments — Crown Zellerbach . . . . . . . . . . 315
VI—l5. Percent Volatile Solids in Sediments - Eastern
PortAngelesHarbor. . 316
VI—16. Salmon Utilization in Port Angeles 327
VI—17. Commercial Salmon Harvest Area 340
VI—l8. Critical Habitat Areas . . . . 348
VI—19. Critical Marine Mammal Areas . . . . . . . . . . 351
VI—20. Movement of Pods of Killer Whales. . . . . . . . 356
VI—2l. Dungeness National Wildlife Refuge Boundaries. . 357
Vu—i. Chlorophyll Levels East of the ITT Rayonier
Diffuser . . . . . . . . . . . . . . . . . . . 377
VII—2. Foodweb of Sand—Gravel/Eelgrass Shallow
Sublittoral Habitat. . . . . . . . . . . . . . . 379
VII—3. Foodweb of Sublittoral Rocky/Kelp Bed Habitats . 380
VII—4. Foodweb of Rocky Littoral Habitats . 381
Vu—S. NeriticFoodweb . . . . 382
VIII—1. Location of Flood Eddies . . 398
VIII—2. Tidal Current Patterns in the Hydraulic Tidal
Model. . . . . . . . . . . . . . . . . . . . . . 400
VIII—3. Growth of Tidal Eddies . . . . . . . . . . . . . 403
VIII—4. Flood and Ebb Tidal Eddies Near Dungeness Spit . 405
VIII-5. Ediz Hook Flood Eddy Observations. . . . . . . . 408
VIII—6. Variance of Current Meter Records. . . . . . . . 410
VIII-7. Computed Kinetic Energy Versus Measured
Variance . . . . . . . . . . . . . . . . . . . . 4].1
VIII-8. SSL and Salinity in Harbor on August 30, 1963. . 413
VIII—9. Mean Surface Currents in the Study Area. . . . . 414
ix

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Page
Cross Sectional Views of the Puget Sound and
Straits
Release and Recovery Positions of Seabed
Drifters . . . . .
Comparison of Nearshore and Midchannel Current
Speeds . . . . . • • • • •
Net Circulation in the Harbor. . . . . . . .
Patterns of Mean Temperature, Salinity, Density
andSSLintheHarbor . . . .
Residence Period Estimated in Hydraulic Tidal
Model Experiment . . .
Countercurrent Traced Using Oyster Bioassay
Test of Effluent Toxicity
Wind, Tide and Currents From September 3, 1975 -
November 3, 1975 . .
Variations in the Countercurrent of Speed, SSL
Concentrations and Frequency of Abnormality.
Dispersion of Oil From A Spill — May 13, 1979.
Seasonal Cycles of Temperature, Salinity,
Density and D.O. . . . . . . . . . . . . . .
Mean Concentration and Cumulative Amount of SSL
in the Harbor. . . . . . . . .
Photographs of Dye Injected into the Hydraulic
Tidal Model At Crown Zellerbach Outfall locations.
Slack, Ebb and Flood Patterns of Effluent From
ITTRayonierOutfall . . . . . . . . . . . .
Recoveries of Onshore Drift Sheets . . . . .
Recovery Positions of Drift Cards Released
April24— 30, 1978. . . . . .
Recovery Positions of Drift Cards Released
July 1. — 2, 1980
Density at Midchannel From the Inner Strait
toPuget Sound’s Main Basin. . . . . . . . .
Isoc].ine Map of D.O. Concentrations -
May 4, 1972. . . . . . . . . . . . . . . . . . .
Isocline Map of SSL Concentrations —
May 4, 1972. . . . . . . . . .
Isocline Map of D.O. Concentrations -
November 1, 1972 . . . . . . . . . .
Isocline Map of SSL Concent atiOfls —
November 1, 1972 . . . . . . . . .
D.O. Readings for STORET Station PAH 003
1967 — 1977. . . . . . .
SSL Readings for STORET Station PAH 003
1967 — 1978. . . . . . . .
Surface SSL and D.O. Linear Regression Line (1970)•
Surface SSL and D.O. Linear Regression Line (1972).
Surface SSL and D.O. Linear Regression Line (1972).
Surface SSL and D.O. Linear Regression Line (1976).
Location of Sampling Stations and Pulpmill
Effluent Discharges. . . . . . . . . . . . .
Selected Locations for Analysis of Variation
In Toxicity to Oyster Larvae . . . . . . . . .
Toxicity Maps . . . . . . . . . . .
Receiving Water Toxicity to Oyster Larvae
1976 — 1978. . . . . . . . . . . . . . . . . .
vill—lO.
Vill—il.
VIII—l2.
VIII—13.
VIII—14.
VIII—15.
vIiI—16.
VIII—17.
VIII—18.
VIII—19.
VIII—20.
vIii—21.
VIII—22.
VIII—23.
VIII—24.
vIiI—25.
VIII—26.
vIII—27.
vIII—28.
vIiI—29.
VIII—30.
VIII—3l.
VIII—32.
VIII—33.
VIII—34.
VIII—35.
VIII—36.
VIII—37.
VIII—38.
VIII—39.
vIII—40.
VIII—41.
415
417
418
421
423
425
426
429
430
433
435
437
440
443
445
446
447
449
451
452
453
454
455
456
458
459
460
461
474
476
477
479
x

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I-B-i. Three Groundwood Systems Employed by Crown
Zellerbach
I—E-1. Secondary Treatment — Crown Zellerbach.
I-K-i. Secondary Treatment Facilities — ITT Rayonier
Page
• . . A—6
• . . A—15
• . • A—37
VI-D-1. Distribution of Subtidal Commercial Clams .
VI-D-2. Distribution of Subtidal Non-Commercial Clams
VI-D-3. Distribution of Subtidal Clam Shell Deposits.
VI-D—4. Legend for Figures VI-D—5 — VI—D-8
VI—D—5. Port Angeles Hardshell Clam Transects
VI-D—6. Green Point Hardshell Clam Transects
VI—D—7. Dungeness Spit and Jamestown Clam Transects
VI—D—8. Dungeness Clam Transects.
VI-E-l. Legend for Figures VI-E—2 — VI-E—4
VI-E-2. Angeles Point and Port Angeles Geoduck Clam
Transects
VI-E—3. Green Point Geoduck Clam Transects. .
VI -E-4. Dungeness Spit and Dallas Bank Clam Transects
VI-F-l. Benthic Invertebrate Sampling Stations
September 30, 1961. . . . . • • . . . . .
VI-F-2. Benthic Invertebrate Sampling Stations
January 19 — 20, 1972
VI-F-3. Habitat Types, Littoral and Sublittoral Sites
Sampled . . . . • . . . . . . . . . . . . .
VI-H-l. Beach Seining Locations Adjacent to ITT Rayonier.
VI-H—2. Beach Seining and Bioassay Stations in Port
Azigeles Harbor . . . . . . . . .
VI-H-3. Location of Nearshore and Intertidal Fish Surveys
Vu—A—i.
VII—A—2.
VII—A—3.
VII—A—4.
VII—A—5.
VII—A—6.
VII—A—7.
VII—A—8.
VII—A—9.
VII—A—l0.
Vu—A—h.
VII—A—12.
Shallow Sublittoral Foodweb — Morse Creek,
Spri.ng. . . • . . . • • • . • • . • . . . •
Shallow Sublittoral Foodweb — Morse Creek,
Summer. . . . • . • • . . . . . . . • . . .
Shallow Sublittoral Foodweb — Morse Creek,
Fall. . . . . . • . . . .
Shallow Sublittoral Foodweb — Morse Creek,
winter • • • ,
Shallow Sublittoral Foodweb — Dungeness Spit,
Spring. • . . • .
Shallow Sublittoral Foodweb - Dungeness Spit,
Suzruner
Shallow Sublittoral Foodweb — Dungeness Spit,
F all • • . .
Shallow Sublittoral Foodweb — Dungeness Spit,
Winter. • . . . . . • . . . . . . • . . .
Meritic Foodweb - Spring. . . . . . . . •
Neritic Foodweb — Sununer .
Neritic Foodweb — Fall
Neritic Foodweb - Winter. . . • . • • .
• . .A— 204
• . •A—2 05
.A—206
• . .A—207
• • •A—208
• . .A—209
•A-.210
.A—211
.A—2].2
.A—213
• . .A—214
•A—215
VIII—42.
VIII—43.
Pulp Production and BOD Loading Via
ITT Rayonier Outfall 007
Volatile Solids and Benthic Organisms in
Bottom Samples
. . •
480
488
. A— 124
• A— 125
• A— 126
.A—127
A— 128
A— 129
• A— 130
•A—131
• A— 136
. A— 137
A— 138
• A— 139
•A—14 3
. A— 144
•A—145
.A—174
.A—l 8 l
A— 176
xi

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LIST OF TABLES
Page
I-i. Historical Summary of Crown Zellerbach Mill. . . 5
1-2. History of Known Discharge Points, Crown
Zellerbach . 8
1—3. Waste Sources Discharging to Port Angeles Harbor 11
1-4. Summary of Violations by Crown Zellerbach. . - . 23
1—5. Historical Summary of ITT Rayonier Mill. . . . . 31
1-6. History of Known Discharge Points, ITT Rayonier. 32
1—7. Miscellaneous Discharge Points, ITT Rayonier . . 34
1—8. Drains Diverted to Primary Treatment System,
ITT Rayonier . 36
1—9. Process Waters Diverted to Uncontaminated Sewer,
ITTRayonier. . . . . . . . . . . . . 38
1—10. SSL and BOD 5 Data for ITT Rayonier . . . . . . . . 48
I—li. History of Modifications to NPDES Permit,
ITT Rayonier . . . . . 56
1—12. Summary of Violations by ITT Rayonier 64
11-1. Port Angeles Surface Water and Ground Discharge
Sources. . • , . . . . . . . . . . . . 83
11—2. Average Annual Discharges of Waste 89
11—3. Estimated Pollutants From Log Rafting. . . . . . . 120
11—4. Summary of Mill Closures, Port Angeles . . . . . . 122
11—5. Toxic Compounds in Mill Effluent . . . . . . . . . 125
11-6. Concentrations of Pulp and Paper Mill Effluent . . 127
11—7. Concentrations of Other Pulp and Paper Mill
Constituents . . . . . 134
11-8. ITT Rayonier Pollutant Sampling - Secondary
Treatment . . . . . . . . . . . . . . . 137
111-1. Characteristic Dimensions and Ratios,
Port Angeles Harbor . . . 156
IV—1. Protected Characteristic Uses of Marine Surface
Waters . . . . . . . . . . . . . . . . . . . . . . 171
IV—2. Water Quality Criteria for Marine Waters . . . . . 172
IV—3. Correlation Between ITT Rayonier Effluent
Dilution and pH Depression . . . . . . . . . . . . 181
IV—4. Water Quality Data From ITT Rayonier Plant
Effluent . . . . . . . . . . . . . . . . . . . . . 199
IV—5. Water Quality Data Collected by the Streeter . . . 200
IV—6. Concentration of Pulpmill Waste. . . . . . . . . . 201
IV—7. Water Quality Data Collected by the Thunderbird. . 203
IV—8. Expected Water Quality Changes . . . . . . . . . . 204
V—l. Acute Effects of SME, SSL and Mechanical
Effluents. . . , . . . . . . . . . . 217
V—2. Sublethal Effects of Sulfite Mill Effluents. . . . 219
V—3. Crown Zellerbach Bioassay Data . . . . . . . . . . 224
V—4. ITTRayonierBioassayData . . . . . . . - . . . .226
V—5. ITT Rayonier Bioassay Data: Sulfite Process . . . 229
V—6. Major Toxic Compounds in Sulfite Pulping
Operations . . . . . • . • . . . . . . 234
V—7. Toxicity of Chlorine to Major Organisms. . . . . . 241
x ii

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Page
VI-1. Major Organic Groups in Port Angeles Harbor. . . . 255
VI—2. Dominant Phytoplankton Species of the Strait . . . 259
VI-3. Dominant Phytoplankton Densities - Port Angeles
H arbor . . . . . . . . 260
VI—4. Macro—algae and Selected Epiphytes - Morse Creek . 266
VI—5. Icthyoplankton Species in Water Near Port Angeles
Harbor 269
vI-6. Zooplankton Species in Waters Near Port Angeles
H arbor . . . . . . . , • , , • • 273
VI—7. Shellfish Surveys in Port Angeles — Dungeness
Area . . . . . • . • • • • 279
VI—8. Shellfish Species Surveyed in Port Angeles . . . . 280
VI-9. Estimated Clam Population and Density 286
VI—lO. Estimated Geoduck Population and Density . . . . . 288
VI—il. Geoduck Population Densities . . . . . . . . . . . 290
VI-12. Number of Species Sampled At Beach Locations . . . 291
VI-13. Crab Catch Data for Dungeness Bay. . . . . . . . . 295
VI—14. Shrimp Catch Data for Port Angeles Harbor. . . . . 295
VI—15. Marine Invertebrate Studies. . 298
VI—16. Benthic and Epibenthic Littoral Invertebrates —
Morse Creek and Dungeness Spit . . . 304
VI—17. Benthic and Epibenthic Sublittoral Invertebrates -
The Harbor to Dungeness Bay. . . . . . . . . . . . 306
VI-18. Benthic Littoral Organisms - Morse Creek and
Dungeness Spit . . . . . . . . . . . . . . . . . . 307
VI—19. Benthic Sublittoral Organisms - Morse Creek and
Dungeness Spit . 308
vI—20. Benthic Organisms and Percent Volatile Solids. . . 313
VI—2].. Percent Volatile Solids in 1964 and 1972 . . . . . 317
VI—22. Abundance of Benthic Organisms - Van Veen Grab . . 319
VI-23. Numbers of Benthic Invertebrates in 1964 and 1972. 320
VI—24. Summary of Fish Surveys — Elwha River East to
Dungeness River. . . . . . . . . . . . 322
VI-25. Freshwater Life Cycle of Salmon and Anadromous
Trout. . . . . . . . . . . . . . . . . . 329
VI-26. Juvenile Salmon Counts in Port Angeles Harbor. . . 338
VI-27. Anadromous Species Composition - Seine Hauls . . . 339
VI—28. Marine Species in Port Angeles Area. . . . . . . . 342
VI—29. Dominant Nearshore Marine Species - Morse Creek
and Dungeness Spit . . . . . . . . . . . . . . . . 344
VI—30. Estimated Commercial Bottomfish Trawl Catch. . . . 347
VI—31. Marine Mammals in Port Angeles Vicinity 352
VI—32. Common Marine Mammal Species in the Strait . . . . 353
VI—33. Occasional Marine Mammal Species in the Strait . . 353
VI—34. Harbor Seal Abundance...... . . . . . . . . .355
VI—35. Marine Birds . . . . . . . . . . . . . . . . . . . 358
VI—36. Concentrations of Selected Marine Birds in the
Inx er Strait . . . . . . 361
VI—37. U.S. Fish and Wildlife Waterfowl Counts. . . . . . 363
VI-38. Waterfowl Observed in Clallam County . . . . . • . 364
VII—l. ChlorophyllData.......... .374
VII—2. Organism Abundance and Diversity . . . 376
xiii

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Page
VIII—l. Observations of Water Properties and Currents
Indicating Countercurrents. . . . . 427
VIII—2. Surface SSL and D.O. Linear Regression. . . . . . 462
VIII—3. Comparison of Toxicity Responses Between Pacific
Oyster Larvae and Rainbow Trout Fry . 465
VIII-4. Chemical Composition of ITT Rayonier Pulpmi].l
Effluent. . . . . . . . . . . . . . . . . . . . . 467
VIII—5. Abnormal Development of Pacific Oyster Larvae
With Associated PRI Concentrations. 472
VIII-6. Clam Densities in Sediments Near Port Angeles . . 490
I-F-i. Overflows and Spills Recorded By Crown
Zellerbach . . . . . . . . . .A—18
I-F-2. Total Months Crown Zellerbach Exceeded Daily
Average BOD . . . . . . . . . A19
I-F-3. Total Days/Month Crown Zeilerbach Exceeded
Daily MinimumBOD 5 . . . . . . . . A—20
I-F—4. Months Crown Zellerbach Exceeded Daily Maximum
scs .
I-F-5. Total Months Crown Zellerbach Exceeded Daily
Average TSS . . . . . . . . .A2l
I-F-6. Total Days/Month Crown Zellerbach Exceeded Daily
Maximum TSS . . . . . . . . . . . . . . . . . . .A—22
I-F—7. Total Days/Month Crown Zellerbach Exceeded Daily
Minimum pH. . . . . . . . . . . . . . .A23
I-F—8. Total Days/Month Crown Zellerbach Exceeded Daily
Maximum pH. . . . . . . . . . . . . . . . . . .
I-I—i. Monthly Averages of SCS and TS at ITT Rayonier. .A-32
I-M—l. Outflows/Spills Recorded by ITT Rayonier. . . . .A-44
I-M—2. Total Days ITT Rayonier Exceeded SSL Moving
Average . . . . . . . . . . . . . . . . . . . . .A53
I-M-3. Total Months ITT Rayonier Exceeded Daily
Average BOD . . . . . . . . . •1 • . . . . .A—58
I—M—4. Total Days/Month ITT Rayonier Exceeded Daily
Maximituin BOD5 . . . . . . . . . . . . .A—59
I—M—5. Total Months ITT Rayonier Exceeded Daily
Average SCS . . . . . . . . . . . . . . . . . . .A—61
I-M-6. Total Days/Month ITT Rayonier Exceeded Daily
Maximum SCS . . . . . . . . . . . . . . . . . . .A—62
I-M—7. Total Months ITT Rayonier Exceeded Daily
Average TSS . . . . . . . . .A—63
I-M-8. Total Days/Month ITT Rayonier Exceeded Daily
Maximum TSS . . . . . . . ‘. . . . . . . . . . . .A—64
I-M-9. Total Days/Month ITT Rayonier Exceeded Daily
I’1inimuxa pH. . . . . . . . . . . . . . . . . . . .A—65
I-M-l0. Total Days/Month ITT Rayonier Exceeded Daily
Maximum pH. . . . . . . . . . . . . . . . . . . .A—66
I l l-A—i. Summary of Currents Observed Less than Several
Days. . . . . . . . . . . .A—68
III—A—2. Summary of Currents Observed for Several Days . .A-73
xiv

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Page
1 11—B—i. Observations of Water Properties. . . . . . . . .A—77
I ll—C-i. Plan View of SSL and Salinity —
September 9, 1962 . A—82
III—C-2. Plan View of SSL and Salinity —
February 3, 1963 A—83
III-C—3. Plan View of SSL and Salinity —
March 8, 1963 A—84
III—C—4. Plan View of SSL and Salinity —
April17, 1963. . . .A—85
III—C—5. Plan View of SSL and Salinity —
April 18, 1963 (a.m.) A—86
III-C—6. Plan View of SSL and Salinity —
April 18, 1963 . A—87
Ill—C- i. Plan View of SSL and Salinity —
June 26, 1963 .A—88
III —C—8. Plan View of SSL and Salinity —
July 27, 1963 . . . . . . . . . . . .A—89
III—C-9. Plan View of SSL and Salinity —
August 30, 1963 . . . . . . . . . . . . . . . .
III—C-i0. Plan View of SSL and Salinity —
September 8, 1963 . . . . . . . . .A—91
Ill—C—il. Plan View of SSL and Salinity —
October 29, 1963 . A—92
III—C—12. Plan View of SSL and Salinity —
December 10, 1963 . . . . . . . . . . . . . . . .A—93
III—C—l3. Plan View of SSL and Salinity —
January 9, 1964 . . . . .A—94
III—D—l. List of Aerial Photographs of Port Angeles
Harbor. . . . . . . . . • • • • • • • • • •A 96
V—A—i. General Categories of Toxic Effects A-99
V-A—2. Techniques Generally Used For Conducting
Toxicity Tests. . . . . . . . . . . . . . . . . A—lOO
V—A—3. Toxicity Tests — Terminology. . . A—lOl
VI-B—].. Saltwater Marsh Vascular Plants From
Dungeness Spit. . . . . . . . . . . . . . . . . A—’ 19
VI-C—1. Percent Relative Abundances of Icthyoplankton
Taxa. . . . . . . . . . . . . . . . . . . . . . A— 12 l
VI—D—l. Clam Density and Substrate Type: Port
Angeles Harbor. • • • . . . . . . . . . . . . . A132
VI-D—2. Clam Density and Substrate Type: Green Point . A—133
VI-D-3. Calm Density and Substrate Type: Dungness
Spit, Jamestown and Dungeness • A—134
VI—E—l. Geoduck Transect Totals, Water Depth, and
Substrate Type: Angeles Point, Green Point and
Dungeness Bay . . . . . . . A—1 4 O
VI—G—1. Benthic, Epibenthic and Pelagic Invertebrates
Sampled . . . . . . . . . . . . . . . . . . . . A—i 47
VI—G—2. Distribution of Marine Life on the Piling
of ITT Rayonier Dock (1961 — 1966). . . . . . . A—172
VI—J—l. Salmon Spawning Use of Streams . . A—182
xv

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Page
VI—J—2. Natural Salmon Escapement Estimates A— i 84
VI—J—3. Artificial Adult Salmon Escapements for
Hatcheries • . . . . . A—l85
VI—J—4. Artificially Reared Salmon Plantings for
Hatcheries A—186
VI-J—5. Freshwater Sport Salmon Catch Data . . . . . . A-l87
VI-J -6. Summaries of Steelhead Catch Data. . . . . . . A-188
VI—K—l. Marine Species Composition — Beach Seine
Hauls • A—190
VI-K—2. Average Number and Biomass of Nearshore
Fish Species — Morse Creek and Dungeness Spit. A-191
VIII—A—l. Concentrations of SSL at Head of Port Angeles
Harbor — November 12, 1964 . . . . . A—219
xvi

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EXECUTIVE SUMMARY
Crown Zellerbach Corporation and ITT Rayonier, Inc., respec-
tively operate a thermomechanical and a sulfite pulpmill near
Port Angeles, Washington. Both mills installed primary treat-
ment facilities for their effluent wastes in 1971 and were re-
quired by Federal Regulations (Permit No. WA 000292-5, Permit
No. WA 000079—5) to install secondary treatment by July 1, 1977.
However, Crown Zellerbach’s secondary treatment was not instal-
led and in operation until October 1, 1978. ITT Rayonier’s
secondary treatment was not operational and in compliance until
October 12, 1979. Thus, secondary treatment equipment at
Crown Zellerbach and ITT Rayonier was operational 15 and 27
months, respectively, following the installation date required
by permits and regulations.
Based on limited monitoring by mill personnal and federal or
state agencies, it can be demonstrated that water quality viola-
tions have occurred. No comparison of the frequency or severity
of these violations can be made between the two mills due to a
severe lack of reporting or monitoring data from Crown Zellerbach.
Many of the water quality violations at ITT Rayonier result from
system malfunctions which cause spills of spent sulfite liquor
or other effluent wastes. According to ITT Rayonier’s own
Monthly Environmental Reports these spills occur with relatively
high frequency. Crown Zellerbach has a more limited reporting
system which has documented spills to some degree.
Effluents from both mills contain a large number of substances
which are potentially toxic to biological organisms. Chemical
and bioassay studies have shown that the concentrations of most
chemical toxicants found in pulpmill waste are significantly
reduced by secondary treatment. Bioassays conducted by Crown
Zellerbach and ITT Rayonier have demonstrated that the primary ef-
fluents from these mills are highly toxic (lethal) to fish and shell-
fish at the 65 percent effluent level. Receiving water bioassay
tests indicate that acute toxicity to oyster larvae results from
xvii

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primary treated effluent from both mills, although toxicity
in Port Angeles Harbor was substantially reduced in 1976, the
year following installation of chemical recovery by ITT Ray—
onier. In-plant bioassay tests from both mills following
secondary treatment installation showed non-lethality at the
65 percent level with survival of fish and shellfish usually
possible at 100 percent effluent for limited time periods.
Data analysis of oceanographic dynamics and hydraulic model
studies have shown that both the ITT Rayonier and Crown Zeller-
bach effluent plumes remain in the nearshore region and that
some effluent from both mills may enter the Harbor. Small
eddy patterns are present which carry effluent in an onshore
direction. These dynamic patterns indicate that Crown Zeller-
bach effluent affects nearshore waters from Tongue Point to
Green Point and that ITT Rayonier effluents- overlap with this
area, affecting outer Ediz Hook, Port Angeles Harbor and waters
as far east as Dungeness Spit or beyond. Mean currents calcu-
lated from a hydraulic model of the Harbor and its approaches
indicate a strong longshore current having a magnitude of
3 X i0 m 3 S 1 . The mills discharge about 2 m 3 into this
transport which implies a maximum dilution of 1:15,000 if
complete mixing were attained. Dilution studies of ITT Rayo—
flier effluent near Green Point, however, show dilution of less
than 1:1000. Most of this dilution occurs rapidly in the near
field region as the plumes rise to the surface waters from the
submerged diffusers. Crown Zellerbach may have higher dilution
ratios than ITT Rayonier due to more energetic water movement
in the Strait of Juan de Fuca.
Whether marine biological populations are being adversely im-
pacted along regular paths of the effluent plumes cannot be
ascertained in many cases with data presently available. Toxi-
city testing shows fewer acute effects in recent years; how-
ever, chronic effects have not been investigated either by
government agencies or the pulp and paper industry. The
Xviii

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toxicants present in these effluents have been shown to move
predominantly across areas of important biological resources
and productivity. In addition, recent studies by the United
States Environmental Protection Agency indicate that primary
productivity in marine waters near the ITT Rayonier outfall
is significantly reduced.
Information on seasonal abundance, populations, health or
biological productivity is not known for most organisms in
the Port Angeles nearshore environments. There is presently
no baseline against which to compare effluent effects. How-
ever, ecological studies of other toxicants (e.g., pesticides,
hydrocarbon products, etc.) has shown that many pollutants
build their concentrations in the ecosystem through the food
chain. Similarly, these studies have shown conclusively that
the absence of obvious acute effects on an organism does not
preclude serious damage to the individual or an entire species
due to long—term chronic effects. In cases where data are
available, productivity, diversity and abundance of naturally
occurring populations have all been shown to decrease, indica-
ting environmental damage.
The amount of environmental damage which may have been caused
through delayed compliance with secondary treatment requirements
cannot be accurately assessed for either of the Port Angeles
pulpmills due to the weakness of the data base. It is clear,
however, that a definite potential for environmental damage
existed during that period, that toxicants were discharged to
the environment, that water quality criteria were not always
met, and that both mills experience spill situations which would
be mitigated by secondary treatment. The report which follows
explores these points in detail.
xix

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I. HISTORY OF PULPMILLS AT PORT ANGELES, WASHINGTON
Growth and development of the logging industry occurred on
the Olympic Peninsula during the late nineteenth and early
twentieth centuries. Early in the twentieth century, in-
creased markets for pulp and paper products led to the esta-
blishment of a number of pulpmills on the peninsula, in Gray’s
Harbor and on the Strait of Juan de Fuca (hereafter Strait).
Port Angeles Harbor (hereafter Harbor) became a natural
focal point for industrial activities, including the pro-
cessing of pulp.
Between 1915 and 1930, three mills began pulp processing
operations at Port Angeles. In 1917, Whalen Brothers (later
acquired by Crown Zellerbach Corporation) initiated a sulfite
and bleached stone groundwood mill near the base of Ediz Hook.
During the same year Fibreboard, Inc. began a sulfite opera-
tion 1/2 mile (.8 km) southeast of the base of Ediz Hook in
the Harbor. In 1930, Olympic Forest Products (later ITT Rayo-
nier) opened a paper grade sulfite mill on the east side of
Port Angeles (Figure I-i).
During the ensuing years, the three mills have undergone
various process changes. In the last decade, state and fed-
eral regulations controlling effluent discharges and water
quality have led to the installation of effluent treatment
systems at the Crown Zellerbach and ITT Rayonier mills. These
regulations may have indirectly contributed to the closure of
the Fibreboard mill in 1970.
The history of each mill is described in detail in the follow-
ing sections. These supply the necessary background for Chap’-
ters II - VII that deal with physical and biological aspects
of aquatic systems in the Harbor and vicinity.

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12:29 12 ’28 12 27
12r26 12f25 12i24 12 f 23
12S’α2 12 f21 12 f’2O
Strait of Juan de Fuca
o 1
Figure i-i. LOCATION OF PULP
I *-C.a.sd dlschsigs CHARGERS AT PORT
AND APPLICATIONS)
MILLS AND
ANGELES,
OTHER INDUSTRIAL
WASHINGTON (NPDES
DIS-
PERMITS
4(09’
Edlz Hook
4801

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The history is described in relation to:
• Processes and operations (including treatment
processes
• Permits and regulations
• Compliance history
The information in these sections was comp J.ed from available
permits, applications and correspondence of the mills. The early
history of each mill, particularly before 1955, is incomplete
due to the lack of a Washington State permit program. Even
after 1955, gaps in the known history exist since the Washing-
ton State Department of Ecology (DOE) does not maintain permit
and correspondence files for more than eight years after a
document’s issuance date and the U.S. Environmental Protection
Agency (EPA) was not created until 1970.
3

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A. CROWN ZELLERBACH
The Crown Zellerbach pulpmill located at the west end of
the Harbor was built in 1917 by Whalen Brothers (Amberg,
letter of October 24, 1977; Crown Zellerbach Corp., no date).
In 1920 the mill was acquired by Washington Pulp and Paper
Company (Crown Zel].erbach , no date). Eventually Crown
Zellerbach merged with the Washington Pulp and Paper Company
(Crown Zellerbach, no date). Throughout its history the
mill has experienced three major changes in its pulping
processes. In conjunction with these process changes, the
mill also made an effort to divert all mill waste effluent
to the Strait and discontinue their discharge to the inner
Harbor. A tabular sununary of Crown Zellerbach’s pulping pro-
cesses and treatment installations is contained in Table I-].
and discussed in the following text. Information contained
in the table was derived from available permits and corres-
pondence currently on file with DOE, Lacey, Washington; EPA,
Region 10, Seattle, Washington and Crown Zellerbach, Port
Angeles, Washington.
1. Process and Operations
Mi’l Operation: The mill initially utilized two paper
machines to produce newsprint from sulfite and stone ground—
wood pulp (Crown Zellerbach, no date). In addition to the
pulp and paper mill facilities, a woodmill built on the mill
complex in 1920 supplied bolts of wood to the stone ground-
wood operation (Hansen 1978). In 1927 to increase the mill’s
production an additional paper machine and more grinders for
the stone groundwood process were installed (Crown Zellerbach,
no date). Throughout the mill’s history newsprint grade pulps
have been produced by the mill; however in the 1960’s the mill
began experimenting with production of directory pulp grades
(Hansen 1978).
4

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Table 1-1. HISTORICAL SUMMARY OF CROWN ZELLERBACH MILL,
PORT ANGELES, WASHINGTON
Began Operation : 1917
Initial Pulping Process : Sulfite and mechanical (bleached stone
groundwood)
Initial Type of Pulp : Newsprint grades
Present Pulping Process : Refiner mechanical (chip groundwood)
Therrnomechanical (chip groundwood)
Present Type of Pulp : Newsprint and directory grades
Major Process Changes and Dates :
1964 Shutdown of sulfite pulpmill
Two stage Refiner Mechanical Process
(RMP) installed
1970 Two additional stages added to the
original RMP
7/77 Replaced Zinc Hydrosu].fite Process
with Ventron Process (Sodium Hydrosulfite)
Three stage RNP installed
11/77 Three stage Therinomechanical Process
(TMP) installed
late 1977 Original RMP converted to Reject Refining
System
Primary Treatment :
Required by: October 31, 1971
Installed by: November 22,1971 (operational)
Facilities: Clarifier
Secondary Treatment :
Required by: July 1, 1977
Installed by: September 15, 1978 (operational by October 1,
1978)
Facilities: Air Activated Sludge
5

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Major PulpmiZ Conversion: A major process change at the
Crown Zellerbach mill occurred in the summer of 1964, when
sulfite pulping was eliminated (DOE files, no date; Crown
Zellerbach, no date). Also during this year a two stage
Bauer double-disc refiner mechanical pulping system (RMP)
was added to the pulping operation allowing the mill to
produce both stone and refiner groundwood puips (Hansen
1978; Crown Zellerbach, no date). In 1970 two additional
stages were added to the RMP to “brush out” the fibers
(Hansen 1978). Refer to Appendix I—A for a comparison of
these two mechanical pulping processes.
In 1976 the mill initiated conversion of the remaining
stone groundwood pulping into two separate operations, three
stage RMP and a Thermomechanical pulping system (TMP) (Hansen
1978) (See Appendix I-A). The stone groundwood process re-
quired intensive labor and operation of the wood mill which
was built in 1920 (Hansen 1978). Installation of the Sprout-
Walden RMP (No. 2 line) and TMP (No. 3 line) eliminated both
of these factors and allowed for improved operations. Crown
Zellerbach throughout most of its history imported kraft
pulp from other mills to mix with their pulps which created
a stronger newsprint product (Rock, personal communication of
April 4, 1979). Installation of the TMP and RMP lines reduced
the amount of required outside pulp from 20 percent to 10 -
15 percent for newsprint grades and from 35 percent to 30
percent for directory grade pulps (Hansen 1978).
Following the conversion to three stage RNP and TMP, the
original Bauer RMP was replaced with a reject refining system
(Hansen 1978). This system handled the rejects from the No. 2
RMP line and No. 3 TMP line in addition to those from the
paper cleaners. For a detailed description of Crown Zeller—
bach’s present RNP, TMP and Reject system refer to Appendix I-B.
6

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Chronology of Discharge Points: Identification of the early
(1920 - 1971) discharge point sources at the Crown Zellerbach
mill was obtained from Application No. 071—OYB-3—000048 (Jan-
uary 29, 1971), its subsequent revisions or additions (Septem-
ber 1971, February 1972, July 1972, September 1972 and July
1973) and Application No. WA 000292-5 (July 2, 1979) currently
on file at DOE, Lacey, Washington (Table 1—2, Figure 1-2).
These applications provide the initial start-up dates only for
those discharge points which were active and were to remain
active as of the application file date. As a result the
initial discharge points 013, 015, 017, 018 and 021 and those
pipes becoming active subsequent to 1920 may not have been
the mill’s only active discharge points, nor were they neces-
sarily active from their start-up date until their designated
rerouting or closure dates. Refer to Appendix I—C for a dis-
cussion on the sludge beds created from those point sources
discharging fiber bearing wastes to the Inner Harbor.
In conjunction with elimination of sulfite pulping, Crown
Zellerbach began a program of gradually rerouting effluent dis-
charge points from the Harbor to the Strait. According to
Aspitarte and Smale (1972) and Moore (1976), Crown Zellerbach
rerouted all. fibrebearing effluents and subsequently all waste
discharge to the Strait in 1964 and 1967, respectively. Appli-
cation No. 071—OYB—3—000048, Permit No. WA 000292—5, Crown
Zellerbach Technical Information Fact Sheet (DOE 1974), DOE
correspondence (Knudson, letter of July 18, 1972; KnudsOn,
letter of November 16, 1972), and studies (EPA 1974) contra-
dict this information and describe discharge pipes 011, 012,
015, 016 (which may not have become active until late 1971)
and 017 as waste dischargers active after 1967 (Table 1-3).
Pipes 013, 018, and 02]. continued to discharge uncontaminated
water to the Harbor; however in August 1973 oil was found to
be in the effluent from 018 (Springer, letter of August 31, 1973).
This discharge continued until November 1973 when it was routed
to the primary clarifier (Knudson, letter of September 14, 1973
and Amberg, letter of November 16, 1973). Although 011 and 012
7

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Table 1-2. HISTORY OF KNOWN DISCHARGE POINTS, CROWN
ZELLERBACH MILL, PORT ANGELES, WASHINGTON
Refer to Figure 1-2.
Date Discharge Points in Operation
1920 013, 015, 017, 018, 021
1927 007,010 began discharging
1935 020 installed
1950 004, 005, 012 began discharging
1/60 009 began discharging
6/60 011 began discharging
1960 006 began discharging
7/65 001 began discharging
3/66 002 began discharging
2/70 008 began discharging
3/70 003, 019 began discharging
11/22/71 001—013 combined into 014. Pipes
014, 015, 0l6**, 017, 018, 019,
020, 021 discharging
11/73 018 rerouted to 014
11/73 — 9/78 014, 017, 020 and 015*, 016*, 019*,
021* only known dischargers
9/78 - present 014, 017, 020 and new 003, only
dis chargers
by 7/79 014, 017 and 020 renumbered to
001, 004 and 002, respectively
*NPDES Permit No. WA 000292-5 implies these dischargers continued
until the installation of secondary treatment but there is no
additional available information to verify this implication.
**No evidence to support exact start-up date for pipe 016, but
it is described in Application No. 071—OYB—3—000048 February 28,
]972.
8

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‘S 0
9?.
0*
‘ 1 6
0
PORT
ANGELES
HARBOR
9 ___
Scale In Meters
* Ref., to Table 1-2
Figure 1-2 Crown Zellerbach Discharge Locations 1920 - 1979
(Application No. 071-OYB -3-000048)
— present
012
1950—71
Lagoon

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were rerouted to the Strait by way of the submerged outfall
in 1971, there is evidence that pipes 015 and 016 may have
continued discharging mill process waste until the installa-
tion of secondary treatment in 1978 (Permit No. WA 000292—5,
DOE 1974). According to the Crown Zellerbach Technical Fact
Sheet (DOE 1974) process mill water and old filter plant
discharge from 017 would eventually be relocated. Presently
017 discharges leakage from the water storage tank and limit-
ed surface run—off (Application No. 000292-5) (Table 1—3).
Installation of primary treatment required the combination
of pipes 001 - 013 into a single submerged diffuser outfall
numbered at that time as 014 (Axnberg, letter of November 22,
1972). This diffuser was located northwest of the mill at a
distance of 1260 feet (384 m) offshore at a depth of 30 feet
(9.1 m) in the Strait.
According to the most recent Crown Zellerbach application
(No. 000292—5), the mill renumbered its four discharging pipes.
The submerged outfall is now 001. The filter plant backwash
(020) and the old filter plant drain (017) are now 002 and 004,
respectively. When secondary treatment was installed a new
discharge 003 was constructed. This point source is the emer-
gency discharge from the main pump station to be used only
in required situations.
Primary Treatment: According to Crown Zellerbach’s state
waste discharge permit No. T-3451, a primary waste treatment
system and a submerged diffuser outfall were to be operable by
October 31, 1971. The primary treatment facilities were re-
quired to remove all floating and settleable solids from the
mill’s waste waters. Such a system was in full operation by
November 22, 1971 (Kendall, letter of November 24, 1971). The
first five months of operation entailed a shakedown period re-
sulting in expected operation of reliable consistent primary
effluent data by March 1972 (Axnberg, letter of February 29, 1972).
10

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Table 1-3. DESCRIPTION OF WASTE SOURCES DISCHARGING
TO INNER PORT ANGELES HARBOR
Source: Application No. 071-OYB—3—000043
Discharge Pipe Description of Waste
011 Wash water from chips containing sawdust
and sediment debris. Discharges to the
lagoon settling pond and overflows to the
inner Harbor
012 Bark from the wood mill. Discharges to
the lagoon settling pond and overflows to
the inner Harbor.
015 Bleach plant t s cooling water, tank seal
water, gland water and floor drains. The
water has a pH range of 2.8 - 3.2. Dis-
charges directly to inner Harbor.
016* Transformer cooling water, boiler blow-
down water, floor drains and roof drains
from the steam plant area. Three discharge
points directly to inner Harbor.
017 Raw water leakage from the old filter
plant, transformer cooling water, old
plant backwash, storm sewers, floor drains
and roof drains. Discharges to the drive
ditch leading to the inner Harbor.
* May not have been operable until 1971, no specific date on its
start up.
11

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Shortly following the treatment systems start-up (December 3,
1971) DOE collected influent and effluent samples from the
mill for analysis (Knudson, letter of December 15, 1971). The
results indicated that substantially all settleable solids (SS)
were removed from the mill’s effluent. Additionally chemical
oxygen demand (COD), turbidity, total suspended solids (TSS),
and total solids (TS) were reduced (Knudson, letter of Decem-
ber 15, 1971). Details pertaining to the operation of the
primary treatment system are contained in Appendix I—D.
Ventron Prooeae: Crown Zellerbach replaced their previous
zinc bleaching technique with the Ventron process by July 1,
1977 (Rock, letter of December 15, 1976; Discharge Monitoring
Report (DMR), July 1977). This procedure combines a 40 per-
cent Boral solution with 50 percent caustic soda and liquid
sulfur dioxide (SO 2 ) to produce 100 percent active sodium hydro—
sulfite and a waste product of sodium borate (Ventron Indus-
tries, no date and Rock, letter of December 6, 1976). Crown
Zellerbach only utilized this bleaching product on their
directory pulp grades (Hansen 1978).
The original zinc bleaching process employed by the mill would
not have allowed Crown Zellerbach to comply with the zinc
concentration levels contained in either the “Interim Policy
Concerning Industrial Discharge of Heavy Metals” (Washington
Water Pollution Control Commission (WPCC) May 13, 1970) (0.5 mg/i
or 10 lbs/day) or their NPDES Permit No. WA—000292—5 (56 lbs/
day ; 25.40 kg/day) (Rock, letter of December 15, 1976). Addi-
tionally large quantities of this bio-accumulative heavy metal
could interrupt the biological activity of secondary treatment
and would interfere with the required toxicity bioassays of sal-
monid fish (Rock, letter of December 15, 1976). Since the ini-
tiation of the Ventron process, zinc has been substantially
reduced from the effluent waste discharge (Refer to Section II,A.1,
Figure 11—7).
12

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Secondar j Treatment: In order for Crown Zellerbach to meet
their final NPDES permit limitations (No. WA—000292—5)
for biological oxygen demand (BOD), secondary treatment or
its equivalent (best practical control technology, BPT) was
to be installed at the mill by July 1, 1977. The permit con-
tained a footnote (a) for the final BOD and other parameters
indicating the limitations for these parameters would be
modified to agree with the final EPA guidelines applicable
to the mill when they were issued (see Section I.A..21. In
October 1975 following Crown Zellerbach’s review of EPA’S
Proposed Phase II Effluent Guidelines (September 5, 1975)
for groundwood mills, the mill concluded that the final BOD
limits contained in Crown Zellerbach’s original NPDES permit
No. WA 000292-5 did not represent BPT (Kott, letter of Dec-
ember 10, 1975; Morris, letter of June 29, 1978). The mill
further concluded that the BOD limits were “legally invalid
(Kott, letter of December 10, 1975).” For these reasons,
the mill suspended further planning and engineering for
secondary treatment facilities (Kott, letter of December 10,
1975). Crown Zellerbach also indicated to DOE they were
planning to seek a judicial stay and modification of the final
BOD NPDES permit requirement (Kott, letter of December 10,
1975)
On January 22, 1976 Crown Zellerbach filed with DOE an
Alternative Application for permit modification of the final
SOD limits or a stay of the compliance schedule for secondary
treatment or its equivalent (Morris, letter of June 29, 1978).
DOE denied Crown Zellerbach’s request for amodification or
stay ( In re: Crown Zellerbach Corp., Port Angeles Mill Docket
No. DE 76—28, (DOE), Order Denying Application for Permit
Modification or Stay filed May 17, 1976). The mill appealed
this decision to the Pollution Control Hearings Board (PCHB).
In settlement of the appeal PCHB issued Stipulation and Order
No. 1039 ( Crown Zellerbach Corp. v. DOE , PCHB No. 1039.
13

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(PCHB) Stipulation filed March 7, 1977, hereafter cited
as Stipulation No. 1039 and Crown Zellerbach Corp. v. DOE ,
PCHB No. 1039. (PCHB Order filed March 15, 1977, hereafter
cited as Order No. 1039). Among other requirements the
Stipulation (No. 1039) revised the secondary treatment
compliance schedule contained in the NPDES permit allowing
the mill to complete construction by September 15, 1978 and
achieve operable compliance by October 1, 1978. Additionally
the final effluent limits were to be revised in accordance with
EPA’S Final Effluent Guidelines for Groundwood (TMP) mills
issued January 6, 1977.
Order No. 1039 remanded NPDES permit No. WA 000292-5 to DOE
with instructions to incorporate the requirements of Stip-
ulation No. 1039 into the NPDES permit. The proper xnodif i—
cations were made to the NPDES permit (April 28, 1977) in
accordance with Stipulation No. 1039 (see Section 1.2) and
on April 27, 1977 DOE issued to Crown Zellerbach an Order of
Compliance (In re: Compliance with NPDES Permit No. WA
000292—5, Crown Zellerbach Corp., Port Angeles, Docket No.
DE 77-197 (DOE), Order of Compliance filed April 27, 1977).
Crown Zellerbach was ordered by DOE to achieve the effluent
limitations and abide by the compliance schedule as specified
in Stipulation 1039.
Despite the fact that the PCHB extended Crown Zellerbach’s
compliance schedule for secondary treatment, this action
only applied at the state level. The NPDES permit issued to
Crown Zellerbach on December 31, 1974 was a contract between
the mill and the federal government (Traina 1976). Even
though the State of Washington (DOE) conducts the NPDES per-
mit program for its state, EPA has the authority to veto
permits when they are inconsistent with the Federal Water
Pollution Control Act requirements and can enforce any viola—,
tions of the permit (Title 33, United States Code, Section 1319).
14

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In order to assure enforcement of Crown Zellerbach’s NPDES
permit, EPA issued a Notice of Violation to the mill and
filed a copy with DOE ( In re : NPDES Permit No. WA 000292—5
for Crown Zellerbach Corp., Port Angeles, Washington No.
X76—12—05—301 (EPA) Notice of Violation filed March
3, 1977, hereafter cited as Violation No. 76—12—05—301)
EPA alleged that Crown Zellerbach had not followed the con-
struction compliance schedule for achieving secondary treat-
ment as contained in NPDES Permit No. WA 000292-5 issued
December 31, 1974. As a result the mill would not be able
to achieve the final July 1, 1977 compliance date. The
violation indicated appropriate enforcement action by the
State of Washington must begin within 30 days following
receipt of the Notice or EPA would take action to enforce
the permit. When the state did not take enforcement action
the U.S. Government upon the request of EPA filed a com-
plaint in the U.S. Western District Court of Washington
( United States of America v. Crown Zellerbach Corp . No.
C77-293M EW.D. Washington], Complaint filed April 25, 1977,
hereafter cited as Complaint No. C77—293M).
The complaint repeated those violations indicated in the
EPA issued Notice of Violation (No. X76—12—05—301) rein-
forcing that footnote (a) referred only to the BOD, SS, and
H limitations and not to the compliance schedule for
secondary treatment or its equivalent (BPT). The complaint
(No. C77—293M) requested the payment of civil penalties by
Crown Zellerbach for violations of its NPDES Permit No. WA-
000292—5. On September 10, 1980 a settlement agreement in
regards to complaint No. C77-293M was made between the United
States Government and Crown Zellerbach Corporation ( United
States of America v. Crown Zellerbach Corp., Port Angeles and Port
Townsend Nos. C77-290M and C77—293M W.D. Washington Settle-
ment agreement filed September 10, 1980). It was agreed by
15

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both parties involved in the settlement that Crown Zeller-
bach Corporation (Port Angeles and Port Townsend) would pay
the federal government $195,000.00 to compensate the civil
penalty claims contained in complaints filed by the United
States Government.
On June 29, 1978 Crown Zellerbach requested from EPA an
extension of its secondary compliance date (July 1, 1977)
to October 1, 1978 (Morris, letter of June 29, 1978). This
request was denied by EPA (Reed, letter of August 25, 1978).
Construction of the air activated sludge facilities began
on December 28, 1977 (Rock, letter of January 12, 1978).
The secondary system was completed by September 15, 1978 and
operative by October 1, 1978 (Kott, letter of October 12,
1978). A discussion of the secondary treatment facilities is
provided in Appendix I-E.
2. Permits and Regulations
The WPCC created in 1945 initiated a Waste Discharge Permits
program in 1955, which allowed issuance of periodic permits
to pulp mills and other industrial dischargers (Pacific North-
west River Basins Commission (PNRBC) 1970). Prior to this
program, the pulp and paper mills in the State of Washington
were not required to obtain permits for discharge of effluent
wastes (PNRBC 1970). The earliest permit presently on file
at DOE for Crown Zellerbach was issued June 6, 1956.
In order to include all the pulping processes of the mill
(sulfite, groundwood and paper production), three separate
waste discharge permits were issued to Crown Zellerbach on
16

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June 6, 1956 (Permit No.s T—90, T—89, 362). The regula-
tions for allowable waste (total volume of cooling and con-
taminated waters) and suspended combustible solids (SCS)
discharged to the Strait, are shown below:
Sulfite
Mi
Maximum Waste Flow
lion gallons/day*
Maximum SCS
Thousand
Material
lbs/day*
2.226
1.6
Groundwood
1.400
13.5
Paper
9.000
21.9
*Conversion:
1 gallon
3.785 liters, 1 lb =
0.4536 Kg
Additional limitations included in each of the three permits
required:
• Combining effluent waste into a single submerged
outfall
• Automatic recording and sampling of effluents
• Preparation of a plot plan locating sewers, identi-
fying source of waste and quantifying the processed
effluent
• Submitting monthly reports on waste flow, SCS, TS
and pulp production to the WPCC
• Treatment of sanitary sewage in a “continuous” main-
tained sewage treatment facility
Permit regulations specific for the three Crown Zellerbach
mill processes included:
• Removal of knotter rejects (sulfite, groundwood)
• Reuse of groundwater pulping effluent (groundwood)
• Practical reuse of white water (paper)
A temporary permit was issued to Crown Zellerbach on May 19,
1961 for the three combined mills (Permit No. T399). The
provisions regarding automatic recording, monthly reports and
treatment of sanitary sewage remained as specified in each
of the previous permits. Stipulations in Permit No. T399
required:
17

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• A maximum waste (total volume of cooling and con-
taminated waters) of 20,000,000 gallons/day
(75,700,000 liters/day) discharged to the Strait
and the Harbor.
• All effluent waste (excluding barker waste) to be
combined into a single outfall and discharged to
the Strait by November 24, 1963.
• Storage of waste cooking liquors, discharged at a
uniform concentration and flow by November 24, 1963.
• Submission to WPCC of engineering plans for auto-
matic waste flow monitoring and approval of plans by
March 1, 1962.
• A detailed report on the mill’s slime control pro-
gram to be submitted to WPCC.
• Lagooning facilities for barker wastes to continue
Beginning May 1961, Crown Zellerbach was required to provide
specific information to the WPCC if operation of the “exist-
ing waste recovery and pollution abatement facilities (Permit
No. T399, May 19, 1961)” was prevented due to unforseen cir-
cumstances.
No available waste discharge permits are on file at DOE, Lacey,
Washington, or EPA, Region X, Seattle, Washington for the
period 1964 — 1967. On December 4, 1967 the WPCC adopted water
quality standards for Washington waters and “...a plan of imple-
mentation and enforcement of such standards (Permit No. T—2895,
May 27, 1968),” (See Section VI.A). Crown Zellerbach’s facil-
ities and waste discharge did not meet the new requirements;
however the mill was allowed to continue discharging through
its existing facilities provided compliance standards be met
within a reasonable time. With this understanding new permit
standards and regulations were issued to Crown Zellerbach on
May 27, 1968. Temporary Permit No. T-2895 provided for:
• A Maximum waste flow (total volume of mill effluent)..
of 17,000,000 gallons/day (64,345,000 liters/day).
discharged to the Strait.
• The design, construction and operation of primary treat-
ment facilities and submarine diffuser outfall;
18

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obtaining final approval of plans by December 31,
1969. Primary treatment will remove all settleable
solids.
• Removal of sludge beds within a 1500 foot (457
meters) radius of the outfall.
• Submission of monthly reports (referred to in this
report as discharge monitoring reports (DMR)) to WPCC
on the daily monitoring of pulp and paper production
(tons), waste flow (gallons), SCS (ibs) and total
solids (TS) (ibs).
• Submission of a detailed report of the slime control
program to WPCC.
• Diversion of sanitary sewage to the City of Port Angeles
sewage treatment plant (STP).
On April 20, 1971 another temporary waste discharge permit
was issued to Crown Ze].lerbach (Permit No. T-3451). The
in—plant slime control program ana sanitary sewage requirement
remained as in the previous permit. Changes stipulated:
• A maximum waste (total volume of cooling and con-
taminated waters) discharge of 15,000,000 gallons/
day (51,775,000 liters/day).
• Operation of primary treatment facilities removing
all floating and settleable solids by October 31,
1971.
• Operation of a deepwater diffuser outfall by October
31, 1971.
• A survey of sludge beds adjacent to the mill to
determine if removal was necessary. Dredging was
required to be complete by September 30, 1974 unless
the mill could prove the beds did not pose a pro-
blem.
• Additions to the parameters required in the previous
permit to include total zinc and BOD in the DMR’s.
• No detectable mercury concentrations to be discharged.
• A maximum zinc concentration at the effluent dilutinn
zone not to exceed 0.1 mg/i by October 31, 1971.
Crown Zeilerbach was issued its first NPDES waste discharge
permit on December 31, 1974 (Permit No. WA—000292—5).
19

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Specified effluent limitation requirements were described
only for submerged outfall 014 (now 001) which emits the
main waste stream. The interim effluent limits (permit
condition S-i) and final effluent limits (permit condition
5—2) allowed pipes 015 — 021 and 017, 020, 021, respectively,
to maintain the effluent levels discharged upon the permit
issuance date, but there were no specific limits designated
in the permit. Outfall 022 was permitted to discharge run—
of f from the sawmill but this structure and outfall was
never constructed (Rock, personal communication of April
4, 1979). Beginning with the date of issuance and lasting
until June 30, 1977 the average allowable BOD, SCS and zinc
interim effluent limits for the submerged outfall (permit
condition S-i) were 18,000 lbs/day (8,165 kg/day),
15,500 lbs/day (2,495 kg/day) and 1500 lbs/day (680 kg/day),
respectively. In addition to maintaining a maximum monthly ave-
rage of the daily discharges for these parameters, the mill
not allowed to discharge on a daily basis a quantity greater
than the designated maximum value for BOD and SCS. The
daily maximum value for BOD and SCS was 25,000 lbs/day
(11,340 kg/day) and 8,000 lbs/day (3,629 kg/day), respec-
tively.
The final effluent limits for 014 (permit condition S—2)
(July 1, 1977 — September 1, 1978) replaced SCS with required
monitoring of total suspended solids (TSS). The average
limit for BOD was 2,100 lbs/day (953 kg/day) and 3,900
lbs/day (1769 kg/day) for TSS. The maximum allowable BOD
and TSS were 5,000 lbs/day (2263 kg/day) and 7400 lbs/day
(3357 kg/day), respectively. The final limitation also
includes a pH range of 6.0 - 9.0 and a maximum allowable
zinc discharge of 56 lbs/day (25.40 kg/day)
20

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secondary facilities or comparable treatment. The permit
included a compliance schedule to enable the mill to achieve
its final effluent limits by July 1, 1977. These included:
• Report of Progress to DOE: March, 1975 and
December 1, 1975.
• Completion of final plans and approval by DOE
March 1, 1976.
• Award of contract: May 1, 1976.
• Start of construction: July 1, 1976.
• Report of construction progress: October 1, 1976.
• Completion of construction: May 15, 1977.
• In compliance: July 1, 1977.
Other significant regulations and provisions of the NPDES
permit required Crown Zellerbach to:
• Monitor toxicity of mill effluent to salmonid
fish beginning July 1, 1975 and report results
to DOE every six months beginning January 1, 1976.
Submit final report April 30, 1978, detailing
results and if necessary remedial measures to
prevent toxicity to salmonid test fish over a
96 hour period in 65% industrial effluent.
• Submit a Spill Prevention, Containment and
Countermeasure Plan by January 1, 1975.
• Prevent a measurable temperature increase (0.5°F)
in the mixing zone of outfall 014 (now 001).
• Provide for foam control facilities.
• Continue reporting yearly the mill’s in-plant
slime control program.
• Submit a plan for disposal of the mill’s solid
waste by June 1, 1975.
• Divert all sanitary sewage to the Port Angeles STP
• Construct an extension to discharge pipe 020 and
have it operable by December 31, 1975
Crown Zellerbach’s NPDES permit (No. 000292-5) was modified
on April 28, 1977 in accordance with Stipulation No. 1039
footnote (a) of the permit’s final effluent limits (permit
condition S-2). According to Stipulation No 1 1039 and footnote
(a) the limits were to be revised in accordance with EPA’s
21

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“Final Amendments to the Interim Final Rulemaking” (42/CFR/
1409-1410, January 6, 1977) applicable to the Crown Zellerbach
mill. The limits for BOD and TSS were modified accordingly:
SOD
Daily Average
lbs/day
Daily Maximum
lbs/day
13,000
7,000
TSS
10,000
19,000
The pH range was revised to 5.0 - 9.0. With the exception
of an extension of the permit expiration date from Septein—
.ber 1, 1978 to December 31, 1979, the remainder of the sig-
nificant regulations and provisions are identical to the
previous unmodified NPDES permit. Additionally footnote (a)
under permit condition S 2 was deleted.
On May 1, 1980 Crown Zellerbach was issued a renewal of NPDES
Permit No. WA-000292—5 that expires March 31, 1981. The
permit requirements were the same as those in the previously
modified permit (April 28, 1977) issued December 31, 1974.
3. Compliance History
Correspondence and reports are necessary to verify the un-
authorized discharges and compliance schedules for installa-
tion and operation of required facilities. The earliest
information found on file at DOE, Lacey, Washington and EPA,
Region X, Seattle, Washington begins in the early 1970’s;
therefore analysis of overflows/spills (Table 1-4 and Appen-
dix I-F,Table I-F—i) and compliance schedules is limited to
the 1970 — mid 1980 time period. With the exception of waste
flow, Crown Zeilerbach’s first effluent limitations for
required monitored parameters (BOD, SCS, TSS, pH and zinc)
occur in NPDES permit No. 000292—5 issued December 31, 1974.
22

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Table 1-4. SUMMARY OF VIOLATIONS RECORDED BY
CROWN ZELLERBACH, PORT ANGELES, WASHINGTON
Time Period
Parameter
Daily
Average
Violations
Daily
Maximum
Violations
Total
Violations
1971-5/80
Overflows!
Spills
N/A
N/A
10*
1/75—5/80
BOD
16
150*
166
1/75—6/77
SCS
1
none
1
7/77—5/80
TSS
5
44
49
7/77—5/80
pH
13**
2
15
N/A - not applicable
*Violatjons not recorded on a daily basis in the appropriate
tables (Appendix I—F) were only counted as one violation.
**Dajly minimum
23

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Violations of these effluent limits as recorded by Crown
Zellerbach are summarized in Tables 1-4 and I-F—i, from
January 1, 1975 to May 31, 1980.
According to available correspondence, at least eight
overflows or spills have occurred at the Crown Zellerbach
mill site from 197]. to May 1980 (Table 1—4, I—F—I ,. From 1973
to mid—1977 four oil spills were reported by Crown Ze].].erbach.
Logbooms were utilized in all cases to contain the spills;
however, the mishap occurring on February 18, 1974 was the
only spill restricted to the inner lagoon. Oil was present in
Port Angeles Harbor during the remaining three incidents.
Four unauthorized discharges contributing SCS to the receiving
water occurred between 1975 and 1976. Three spills (July 24,
1973; August 2, 1973; March 10, 1975) discharged directly
to the Harbor. On February 2, 1976 42,000 gallons (158,970
liters) was directed to the inner lagoon area ( rable 1—4).
Operation of the primary treatment system and submerged
diffuser outfall began approximately 3 weeks subsequent (Nov-
ember 22, 1971) to the required October 31, 1971 permit dead-
line. Also at this time the mill was to limit its discharge
of zinc so that its concentration did not exceed 0.10 mg/i at
the dilution boundaries in the vicinity of the diffuser. The
DOE conducted a receiving water quality survey on February 23,
1972 to test for this zinc standard (Knudson, letter of Dec-
ember 15, 1971; Knudson, letter of April 19, 1972). The
results showed the mill’s outfall met the zinc standard (Knud-
son, letterofApri]. 19, 1972).
In accordance with NPDES permit condition S.6.h., Crown
Zellerbach submitted to DOE their required plans for an exten-
sion of their filter plant backwash discharge (020) on
24

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May 12, 1975 (Nadig, letter of May 12, 1975). These plans
were approved by DOE on June 24, 1975 and construction was
complete by December 29, 1975 (Behike, letter of June 24,
1975; Kott, letter of December 29, 1975).
NPDES permit condition S6.a required Crown Zellerbach to
conduct specific toxicity monitoring during a two year period
and submit a report by April 30, 1978. The required bio—
assays were conducted by the mill and submitted to DOE every
6 months (Cormack, letter of December 30, 1975; Young, letter
of June 28, 1976; Cormack, letter of December 31, 1976;
Cormack, letter of June 30, 1977; Cormack, letter of December
28, 1977; Cormack, letter of May 15, 1978; Corinack, letter
of December 14, 1978; Cormack, letter of May 23, 1979; Cormack,
letter of July 2, 1980). A final report on the results was
submitted to DOE on May 15, 1978 as required (Cormack, letter
of May 15, 1978).
Two additional requirements contained in the NPDES permit
condition 5.6. pertain to solid waste and in-plant slime
control programs. The mill complied with the required sub-
mission to DOE of solid waste disposal plans. Such plans
were submitted on May 20, 1975 (Nadig, letter of May 20, 1975).
It appears from the available correspondence the mill also
complied with its yearly submission to DOE of the mill’s
in-plant slime chemical program (Morgan, letter of December
13, 1976; Morgan, letter of January 10, 1978).
As of July 1, 1977 the mill was required to limit its daily
maximum zinc discharge to 56 lbs (25.4 kg). In order to
achieve this limitation the mill was required to install
alternative bleaching facilities. The mill complied with
this permit requirement by installing the ventron process.
From July 1977 to May 1980 the required 24 hour composite
25

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sampled monthly has shown no violations of the maximum 56
lbs/day (25.4 kg/day) effluent limit, and only on ten occa-
sions has the mill exceeded 10 lbs/day (Figure 11—7).
Since the mill did not install their secondary facilities
until 13½ months after the required July 1, 1977 date,
Crown Zellerbach violated their daily BOD requirement
during the entire period (Table I—F-2). The daily maximum
values, whenever available, indicate violations throughout
the month for July - November 1977 (Table I-F—3). Maximum
violations also occurred from December 1977 - August 1978.
Subsequent to the installation of secondary treatment only
7 violations of the required daily maximum BOD have occurred
(Table I—F—3).
In addition to monitoring BOD, the mill was required to sub-
stitute TSS analysis for SCS. Despite the fact Crown Zeller-
bach had not izfstalled secondary treatment facilities, the
mill did comply with monitoring of TSS beginning July 1,
1977. From July 1977 to May 1980 the mill violated their
average TSS requirement on 5 occasions (Tables 1-4 and I-F-6).
Utilizing available data the allowable daily maximum limit was
violated 44 times during this period (Tables 1-4 and I—F-7).
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B. FIBREBOARD
The Fibreboard Paper Products Corporation operated at Port
Angeles during the period 1917 - 1970 (U.S. Department of
Interior (USD1) 1967). Due to its early closure date, there
is only one known permit for the mill. The majority of in-
formation regarding the mill’s processes and effluents de-
rives from several in-plant surveys made during the 1960’s
and scattered references in other documents (WPCC et al.
1964 (a) ; wPCC et al. 1964(b) ; Moore 1976 and USD1 1967).
1. Processes and Operations
The Fibreboard pulp mill was located near the west end of
Port Angeles Harbor. The mill utilized both stone ground-
wood and ammonia based sulfite pulping processes. The mill
also repulped variable quantities of waste paper (USD1 1967).
The major process components were a mechanical log barker
for both pulping processes, beaters and groundwood pulping
machines, a bleach plant, an acid plant and digesters for
the sulfite process (USD1 1967). The plant discharged fiber,
cooling water and process waste waters directly to Port Angeles
Harbor from two to five discharge points (USD1 1967). These
waste waters were not treated in any way.
The Fibreboard mill, ceased discharges in November 1970. Some
correspondence and reports refer to official closure occurring
in January 1971, probably due to a time lag after mill shut-
down before all operations could cease (Moore 1976).
2. Permits, Regulations and Compliance
The only wastewater discharge permit on file for Fibreboard was
issued May 27, 1968 and expired April 1, 1971 (Permit No. T2865).
27

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This temporary permit allowed continuance of discharged
wastes provided the mill eventually comply with the December
4, 1967 water quality standards.
Fibreboard was allowed a maximum daily waste discharge (total
volume of mill effluent) of 5,654,000 gallons/day (21,400,390
liters/day) to Port Angeles Harbor. Additional permit require—
ments included:
• Installation of primary treatment and submarine outfall
by September 30, 1970.
• Removal of sludge beds no later than 6 months following
primary treatment installation.
• Monthly monitoring reports for pulp and paper production,
waste flow, SCS, TS and BOD.
• Reporting of in—plant slime control program.
Available records indicate that the Fibreboard mill shutdown
of operations roughly coincided with the requirement for in-’
stalling primary treatment. Correspondence indicates primary
treatment installation was delayed as a result of internal
financial difficulties (Simon, letter of July 20, 1970).
Whether shutdown was in fact caused by insufficient capital is
purely conjecture, there being no available records on the
subject.
28

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C. ITT RAYONIER
Rayonier, Inc. began operations as Olympic Forest Products
in Port Angeles in 1930. Later, Olympic Forest Products
combined with two other forest product companies under the
name Rayonier, Inc. Still later, the company was acquired
by the International Telephone and Telegraph Corporation, and
became ITT Rayonier, Inc. (Federal Water Pollution Control
Administration (FWPCA) 197)). General historical summaries
of known pulping processes, treatment installations and dis-
charge points are summarized in Tables 1—5 and 1—6.
1. Processes and Operations
Initial Pulp Mill Operation: The mill’s initial pulping pro-
cess involved papergradesulfite production (Hawks 1975). By
1935 ITT Rayonier installed appropriate equipment to also pro-
duce dissolving grade pulps (Hawks 1975). Throughout its his-
tory ITT Rayonier has produced a variety of paper grade and
dissolving grade pulps; however dissolving pulp grades present-
ly account for approximately 66% of the mill’s annual produc-
tion (Bodien, personal communication of August 20, 1980).
Each type of dissolving pulp produced by the mill can be
placed into one of the following categories: acetate grade,
viscose grade, cellophane grade and nitration grade (Button,
letter of January 19, 1978). Refer to Appendix I—G for general
information on the sulfite process and a comparison of the
paper grade and dissolving grade pulps. Appendix I-H contains
specific information on dissolving grade puips.
Chronology of Discharge Points: Identification of ITT Rayon—
ier’s initial discharge pipes and their respective locations
29

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is limited to information contained in Application No.
WA 071—OYB—2-000038 (June 30, 1971) and subsequent revisions
of May 1, 1972 and April 24, 1973 (Figure 1—3). These
applications provide the initial start—up dates only for
those discharge points which were active as of the appli-
cation date. The accompanying transmittal letter (Scofield,
letter of June 30, 1977) to Application No. WA 071-0Y13—2—
000038 (June 30, 1971) indicates 16 minor outfalls of steam
trap locations discharged mill waste water either directly
into the harbor or into a tributary flowing to the harbor
(Table 1—7). Initially the United States Environmental
Protection Agency (EPA) indicated discharge permits were
needed for 5 of these point sources (Walters, letter of Jan-
uary 24, 1972). It was finally decided by EPA that only one
of the discharges necessitated a permit (006 filter plant back-
wash) which was incorporated into the revised application (No. WA-
071—OYB - 2—000038, May 1, 1972). Three of the 16 discharge
sources were to be routed to the primary treatment system
and the flow rate, pH, temperature and total solids of the
caustic unloading line were required to be monitored in
place of a permit (Table 1—7) (Hawks, letter of February 8,
1972). No further information is provided on the early history
of these 4 additional mill waste point sources. As a
No further information is provided on the early history of
result pipes 001, 002, 003, 004, 005 and 006 may not have
been the only active waste discharging points during the
mill’s early history, nor did these 6 point sources necessarily
remain active throughout the period of 1930 to 1972.
Complying with a federal stipulation ( United States of
America v. ITT Rayonier, Inc. , Civil No. 9586, (WD Washington),
Stipulation filed March 30, 1971, hereafter cited as Stipula-
tion No. 9586), ITT Rayonier constructed a submerged outfall
(007) by August 1972 (USEPA 1974).
30

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Table 1—5. HISTORICAL SUMMARY OF ITT RAYONIER INC.,
PORT ANGELES, WASHINGTON.
Began Operation : June 1930
Initial Pulping Process : Calcium base sulfite*
Initial Type of Pulp : Paper grades
Present Pulping Process : Ammonia base sulfite
Present Type of Pulp : Dissolving grades and paper grades.
Process Changes and Dates :
1935 Initiated production of dissolving
grade puips.
by 12/74 Chemical Recovery System was built.
2/76 Chemical Recovery System’s first month
of compliance.
Primary Treatment :
Required by: September 30, 1972
Installed by: September 20, 1972 (achieved compliance
with permit)
Facilities: Clarifier
Secondary Treatment :
Required by: July 1, 1977
Installed by: October 12, 1979 (achieved compliance
with permit)
Facilities: Deep Tank Aeration/Dissolved Air Flotation
(DTA/ DA?)
* Calcium base sulfite mill was operating in 1957, indicating
it was the initial process (Petersen and Gibbs 1957)
31

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Table 1-6. HISTORY OF KNOWN DISCHARGE POINTS, ITT
RAYONIER, INC., PORT ANGELES, WASHINGTON
Refer to Figure 1—3
Date Discharge Points in Operation*
1930 — 8/72 001, 002, 003, 004, 005, 006
9/30/72 — 1/21/73 003A, 005, 006, 007
(previous 003 renumbered to 003A)
1/22/73 — 12/31/74 003A, 006, 007
(005 diverted to 007)
1/1/75 — 9/2/75 003A, 007
(006 diverted to 007)
9/3/75 - present 007
(003A diverted to 007)
1/18/78 007 renumbered to 001
* According to 1972 correspondence, four additional point
sources were discharging process waste to the Harbor.
Data on their start—up dates is not available.
32

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ANGELES
HARBOR
001
1978— pr.s.nt
Scal. in Mstsrs
Figure 1—3
IT’r—Rayonier Discharge Locations 1930 - 1979
(Application 071—OYB—2—000038)
PORT
33

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Table 1-7. THE MISCELLANEOUS DISCHARGE POINTS LOCATED AT ITT RAYONIER, INC.,
PORT ANGELES, WASHINGTON IN 1971
Source: Scofield, letter of June 30, 1971
MINOR DISCHARGE POINTS STEAM TRAPS —_____________
1. Ditch north of mechanical barker conveyor, carries 1. Discharge from steamline to generating plant.
log wash water and yard area drain (south of hy— Drains into Ennis Creek. A negligible amount
draulic barker operating station) runs westerly of clear condensate.
into log pond. This will be included in the Pri-
mary Treatment Project. 2. Discharge into Ennis Creek from beaterinan’s
heater. Nagligible amount of clear condensate.
2. Power house drain due west of power house to log
pond just south of mechanical barker conveyor. 3. Drain from battery charging room heaters. It
Carries miscellaneous surface drains in the power discharges onto ground, and is a negligible
house area. Clear water only, amount of clear condensate.
3. Filter plant backwash drain into Ennis Creek. 4. Drain from heater in strip treat room. Dis-
charges a negligible amount of clear conden—
4. Road and storm drains from parking area by main sate into Ennis Creek.
office and garages. Discharges into Ennis Creek
just north of bridge. Storm water only. 5. Drain from warehouse truckers lunchroom. A
negligible amount of clear condensate discharges
*5 Tank car unloading pit and other surface drains from onto rock east of warehouse.
dO 2 generator plant area. Discharges into Ennth
Creek from east. Flow is negligible. 6. Cooling water from air dryers at chlorine car
R.R. spur. A small amount of clear water dis-
6. Two lines, used in rare emergencies only, to carry charges onto the beach.
weak solutions of C102 and SO 2 , respectively. Both
drain to Ennis Creek. 7. Glue room heater trap discharges to beach north
of warehouse within outfall foam boom.
*7, Beater drain which discharges onto ground. The
beater re—slushes dried scrap pulp for re-use. No **8. Drain from caustic unloading line tracer.
chemicals are involved—-only water and scra 1 . Discharges negligible amount of clear conden-
sate into bay at caustic unloading station.
*8. Laboratory sink drains, discharging a small but
variable volume of miscellaneous laboratory wastes
into Ennis Creek east of finishing room.
* Diverted to primary treatment facilities ** Required to monitor flow, pH, temperature and
Source: Scofield, letter of June 30, 1971 total solids in lieu of securing a permit.

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All residual wastes* and no more than 15% SSL solids
generated by the mill were to be discharged through the
submerged outfall by September 30, 1972 (Stipulation
No. 9586). The line extends 7000 feet (2134 m) northeast
from the mill and accommodates an additional 970 foot
(296 m) diffuser extending north from the pipeline’s
terminus (Application No. 071—OYB—2-000038, May 1, 1972).
During this same time period the mill also installed
primary treatment facilities resulting in a combining and
rerouting of several discharges to the newly installed
submerged outfall (007) (Hawks, letter of July 5, 1972;
Hawks, letter of September 17, 1972; Gray, letter of Aug-
ust 24, 1973). Three miscellaneous sewers (4,5,6) were
diverted to the primary clarifier (Table 1—7) (Hawks,
letter of February 8, 1972). As of September 1972 outfalls
001, 002, 004 and the bleach plant effluent from 003 were
rerouted to the primary treatment system (DMR, September
1972; Application No. WA—071—OYB—2—000038, May 1, 1972;
Hawks, letter of September 17, 1972). Outfall 003 was
renumbered to 003A and continued to discharge SSL from the
digesters and blowpit washings (Application No. WA-071-
OYB.—2—000038, May 1, 1972).
Wastes from five minor drains were diverted to the primary
treatment system between late 1972 and early 1973 (Hawks,
letter of August 25, 1972; Hawks, letter of December 7,
1972; Huleman 1972; DMR February 1973). These additional
suinps are included in Table 1-8 . With the exception of
Sewer E (005), there is no information currently available
to indicate the waste discharge diverted to and from these
collecting suxnps represents any of the remaining 15 miscel-
laneous discharge point sources listed by ITT Rayonier
(Table 1—7); however some of these sumps may have consolidated
wastes from previous outfalJ.s 001, 002, 003, and 004.
*wastes generated in the mill process except cooling water
and waters used to clean filters or screen in the water
purification process
35

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Table 1-8. FIVE MINOR DRAINS DIVERTED TO THE PRIMARY TREATMENT SYSTEM,
ITT RAYONIER, INC., PORT ANGELES, WASHINGTON
Source: Hawks, letter of August 25, 1972
STATION FUNCTIONS PUMP SIZE
Cordwood Deck Pump Station Log wash
(pumps to Brinkley screen) Yard drains from cordwood side
Drains from N. end power house
Sewer “E” Pump Station Blow pit drains to ground 1400 gpm @
(when approved for construction Digester building drains to ground 40 ft. head
will pump to Brinkley screen) Acid plant drains to ground
Power house drains
Some turbine cooling water drains
Boiler blowdown drains
Woodyard drainage
Bark washer drainage to ground
Broke Pulp Pumping Station
( pumps directly to solids 30”
force main)
C10 2 Pump Station 350 gpm @
(when approved for construction, 87 ft. head
will pump directly to clear 30”
force main)
Acid Plant Pump Station Pure cell filter drain 3450 gpm @
(when approved for construction, Strong acid plant drains 47 ft. head
will pump directly to clear 30” Acid Plant cooling pond overflow
force main)

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During 1975 the two additional discharging outfa].ls (006 and
003A) were rerouted to the submerged outfall. The filter
plant backwash was diverted to 007 as of January 1, 1975
(DMR January 1975). On September 3, 1975 pipe 003A which
discharged unincinerated SSL produced by the mill was rerouted
to the submerged outfall (Rogstad, letter of July 25, 1975).
ITT Rayonier indicated in their NPDES application filed
January 18, 1978 (No. WA-000079—5) that outfall 007 was re-
numbered to 001. The installation of secondary treatment
facilities did not introduce any new or additional permitted
discharge point sources into receiving waters; however
several streams within the mill were rerouted to reduce the
influent waste flow requiring treatment from 42 million gal—
ions per day (mgd) to 30 mgd (DOE 1978). This flow reduction
was achieved by segregating or recycling mill waste waters.
Those streams consisting of non-contact cooling water or less
than 0.3 lbs/1000 gallons (.14 kq/3785 1) of suspended com-
bustible solids (SCS) with flO biological oxygen demand (BOD)
were removed from their existing solids sewer and strong sewer,
and routed to a newly constructed uncontaminated sewer for
discharge directly to outfall 007. The process waters
diverted to the uncontaminated sewer are described in Table
1—9 (Rogers, letter of May 17,1978). Recycling of wastes
was achieved by routing effluents to the pulp screening
operations and bleached decking showers (Rogers, letter of
May 17, 1978).
A comparat ive schematic history (1970 — 1980) of the
effluent source for each mill outfall is shown in Figures
1—4, 1—5, and 1—6.
Frimar j Treatment: In late 1961 the Governor of Washington,
Albert D. Rose].lini, requested assistance from the U.S.
37

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Table 1-9. PROCESS WATERS DIVERTED TO THE UNCONTAMINATED
SEWER, ITT RAYONIER, INC., PORT ANGELES, WASHINGTON.
Source: Rogers, letter of May 17, 1978
Process Wastewater
Flow
MGD
pH
BOD
lb/day
SCS
lb/l000 gal
1.
SSL Evaporator Surface
Condenser Cooling Water
4.5
6.5
0
0
2.
Recovery Boiler I.D. Fan
Bearing Cooling Water
0.4
6.5
0
0
3.
Power House Turbine Oil
Cooling Water
0.9
6.5
0
0
4.
Post 2nd C1O2 Stage Washer
Effluent
3.0
2.2
700
0.12
5.
Cl02 Generator Process
Waste & Cooling Water
0.3
1.4
0
0
6.
Limerock Scrubbing Tower
Effluent
2.3
2.5
100
0
7.
Blowpit Recovery Tower
Effluent
0.8
2.5
100
0
38

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Figure 1—4.
SCHEMATIC OF WASTE SOURCES (1970), ITT RAYONIER, INC., PORT ANGELES, WASHINGTON*
Source: Application No. T—3373
*Correspondeflce indicates filter plant badkwash (006) was discharging to Ennis
Creek previous to 1972 (Scofield, letter of June 30, 1971)
OUTFALL A
001
BLEACH
PLANT
SCREEN
PLANT
DIGESTER
BUILDING
AND
BLOWPITS
ACID
PLANT
POWER
HOUSE
AND
WOODMILL
OUTFALL OUTFALL OUTFALL OUTFALL E
004
003 002
005

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Figure 1-5. SCHEMATIC OF WASTE SOURCES C1977), ITT RAYONIER, INC., PORT ANGELES, WASHINGTON
WOOD
er, 1977
CHIPPING
SUL 1 UR J___ _____ Rayoni
ATM. ATM.
AMMONIA
CAUSTIC I
____ MACHINE
ACID PULPING ____
. DIGESTERS LIOUOR SCREENING BLEACHING DRYING FINISHING
MEG. SEPARATION
ATM. _____ 1 1 1
SOLIDS
SEWER
MISC.
EVAPORATION PRIMARY PRIMARY
__,,. SLUDGE TO
AND TREATMENT INCINERATION
BURNING
I
_____________________________________ ________________ STRONG SEWER
UNTREATED MILL DISCHARGE
NO. 001
WATER TO SANITARY
MILL SEWER
TREATED
EL A TER WA R TO
___ I I
MILL TO
MILL
RIVER TREATMENT
WATER FILTER PLANT BACKWASH
PORT ANGELES
SUPPLY MUNICIPAL
____________ PORT ANGELES WATER SUPPLY
MUNICIPAL
WATER SUPPLY

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Outfall No. 001
Figure 1-6. SCHEMATIC OF WASTE SOURCES (1980), ITT RAYONIER, INC.,
PORT ANGE lES, WASHINGTON
Source: Bill Yake, letter of February 14, 1980
Flow
L 1
Dissolved
Air
FiotstlCfl
Clarlti.fS
.
0.
El
41

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Department of Health Education and Welfare (HEW) to
aid in the prevention and control of pollution in Puget
Sound and its tributaries and estuaries. As a result of
the request a conference under the provisions of the
Federal Water Pollution Control Act (P.L. 660) was con-
vened on January 16 — 17, 1962 (Conference on the Matter
of Pollution of the Navigable Waters of Puget Sound, the
Strait of Juan de Fuca and their Tributaries and Estuaries;
hereafter Puget Sound Enforcement Conference). The con-
ferees concluded that some industries, particulary seven
pulp and paper mills were not providing adequate facili-
ties or practices to control pollution (FWP( A 1970).
A joint Federal - State investigation and study was re—
commended to study the pollution problem. The results of
the studies were published in the “Pollutiona]. Effects
of Pulp and Paper Mill Wastes in Puget Sound (USD1 1967) .“
A second Puget Sound Enforcement Conference was convened
on September 6 - 7 and October 6, 1967 to recommend
necessary steps for pollution abatement (FWPCA, 1970).
The State of Washington adopted the recommendations as
part of the “Regulation Relating to Water Quality Stan-
dards for Interstate and Coastal Waters of the State of
Washington and a Plan of Implementation and Enforcement
of Such Standards” (FWPCA 1970 and Docket 67-2 filed
December 4, 1967 adopted January 3, 1968). The recom-
mendations adopted by the conferees were included in the
permits issued to each pulp mill (FWPCA 1970).
Two recommendations included in Permit No. T-2867 issued
to ITT Rayonier on March 30, 1970 by the Washington State
Water Pollution Control Commission (WPCC) included the
42

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requirement for primary treatment and a submarine outfall
with diffuser by September 30, 1972 and June 30, 1974,
respectively. ITT Rayonier contested certain provisions
of this permit and had also failed to secure the proper
discharging permits from the Corps of Engineers (FWPCA
1970). This led to federal Stipulation (No. 9586) result-
ing from a complaint filed by the U.S. Government concerning
the mill’s discharge without proper permits. The stipula-
tion required the mill to complete both primary treatment
and a submerged diffuser outfall by September 30, 1972.
Installation was completed on ITT Rayonier’s primary
treatment facilities on September 15, 1972. Operation
of the treatment facilities began on September 20, 1972
and has continued to the present (Hawks, letter of Sept-
ember 17, 1972). For the first several years, operational
problems continued to cause breakdown or failure of the
primary treatment system at relatively frequent intervals
(ITT Rayonier, Monthly Environmental Reports (MER), May
1974, February, April, May, July, August, November, Decem-
ber 1975, February, March, October, December 1976, and March,
April, June, September, October, December 1977; Monthly
Environmental Summary (MES), April, May 1976 and May 1977).
After 1977 these failures became less frequent (Refer to
Appendix I—M, Table I—M—1). Details of the primary treat-
ment system and the effect of the system on the ITT Rayonier’s
discharge of total solids are discussed in Appendix I-I.
The various controversies surrounding dredging of the ITT
Rayonier sludge beds are discussed in Appendix I-J.
Secondary Treatment: In order to achieve the e f1uent
limitations for BOD and Total Solids (TS) contained in
Permit No. WA—000079—5 issued August 30, 1974 (Special Con-
dition S3), the mill was required to place in operation a
43

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waste treatment facility comparable to secondary treatment
by July 1, 1977. To assure operation of these facilities
by the specified date, a compliance schedule was included
in Special Condition $4 of the Permit (No. WA—000079—5
issued August 30, 1974) (See Section I.C.2). ITT Rayonier
did not comply with this schedule and on March 3, 1977
the EPA Regional Administrator issued to ITT Rayonier a
Notice of Violation ( In re : NPDES Permit NO. WA—000079—5
for ITT Rayonier, Inc., Port Angeles, Washington, No.
X76—12-08-30l, (U.S.E.P.A.) Notice of Violation filed
March 3, 1977)
The violation indicated that if appropriate enforcement action
was not taken by the State of Washington within 30 days, the
PEA could take legal action to enforce the permit requirements.
On April 27, 1977 the Federal Government filed a complaint
( United States of America v. ITT Rayonier No. C77-289M (W.D.
Washington) hereafter cited as Complaint No. C77—289M) which
resulted in an order granting the Federal Government a Motion
for Summary Judgement ( United States of America v. ITT
yonier , Inc . No. C77—289M (W.D. Washington) and an Order
Granting Motion for Partial Summary Judgement (Injunctive
Phase) filed October 5, 1977, hereafter cited as Order No.
C77-289M). ITT Rayoriier was ordered to achieve the final
effluent limitations contained in Permit No. WA 000019—5 no
later than 20 months from October 5, 1977 (June 5, 1979). In
the fall of 1977 the mill appealed this decision to the United
States 9th Circuit Court of Appeals. That court reversed the
Su timary Judgement Order in No. C77-289M on September 15, 1980
( United States of America v. ITT Rayonier, Inc . No. 77—3672
(9th Circuit Court of Appeals) filed September 15, 1980,
hereafter cited as No. 77—3672).
The preliminary plans for the waste abatement facilites were
submitted to the Washington State Department of Ecology
(DOE) on January 13, 1978 and field construction commenced
by February 1978 (Burkhalter, letter of June 15, 1979,
44

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Baizar 1978). The final plans and specifications for second-
ary treatment facilities (Appendix I—K) and disposal of
secondary waste sludge were submitted to DOE on March 30, 1978
and January 17, 1979, respectively (Burkhalter, letter of June
15, 1979). Conditional approval of the final plans was provided
by DOE on May 22, 1978 (Burkhalter, letter of May 22, 1978).
Final approval of the plans and s ecifications was granted
by DOE on June 15, 1979 (Burkhalter, letter of June 15, 1979).
Following a meeting and review of the mill’s progress in
completing its secondary treatment system, John Biggs, the
presiding Special Master, recommended to Judge McGovern
that the mill’s secondary treatment compliance date be
extended to October 10, 1979 (Biggs, letter of June 25, 1979).
ITT Rayonier’s air activated secondary facilities achieved
compliance on October 12, 1979; however compliance has not
been maintained (see Section I.C.3).
Presently the disposal of the secondary sludge generated from
biological treatment is mixed with primary sludge, dewatered
and buried in the Shotwell gravel quarry site but the life
expectancy of this site (June 30, 1981) has required the mill
to view other sludge handling alternatives (Berner, letter
of July 10, 1979). ITT Rayonier personnel indicated that
before June 1981 they would examine long term alternatives
for the handling of sludge. To eliminate sludge land disposal
the mill proposed the Carver/Greenfield system which aids
in removing excess water from the sludge to allow for burning.
The mill is presently in its final stages of installing
this system (Bodien, personal communication of August 22, 1980).
Chemical Recovery: ITT Rayonier’s Permit No. T—2867
(March 30, 1970) required implementation of a chemical
recovery system by June 30, 1974 to remove 80 percent of the mill’s
solids or limit discharge to 370,000 lbs/day of SSL solids from
the effluent (FWPcA 1970). The mill contested these provisions of the
45

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permit and continued to operate without the proper waste
discharge permits (FWPCA 1970). This lead to federal
stipulation (No. 9586) requiring the mill to collect and
incinerate 85 percent of the SSL solids produced by the
mill. The furnace was required to incinerate no less than
90 percent of the mill’s generated SSL solids. These
facilities were to limit the SSL .solids discharge to 15
percent of the total SSL solids generated by the mill
(averaged over a 14 day period) and divert this discharge
through the submerged outfall (Stipulation No. 9586).
Operation was required to commence on June 30, 1974 and
attain continual compliance by December 31, 1974.
The mill’s first National Pollutant Discharge Elimination
System Permit (NPDES No. WA 000079—5), issued August 30, 1974,
specified construction completion and operable compliance by
December 1, 1974 and April 1, 1975, respectively. Due to
various labor strikes, delays in equipment deliveries and
mechanical start-up problems, the permit was modified on
two occasions (January 24, 1975 and October 22, 1975)
resulting in a final chemical recovery compliance date of
December 1, 1975 (Behlke, letter of January 24, 1975;
Tucker and Starr, letter of September 25, 1975; Smith,
letter of October 15, 1975). Despite the permit modifica—.
tions, Stipulation, Civil No. 9586, has not been dismissed
by the Courts and require a December 31, 1974 compliance
deadline.
According to ITT Rayonier correspondence (NER May 1974),
l1 permits for construction of the SSL lagoon were re-
ceived and construction was begun in June 1974. The chemical
recovery system consisted of a lagoon for recovery of SSL,
a stripper, a cooler—absorber, multiple effect evaporators
(ME evaporators), vapor recompression evaporators (VRC)
and turbines, dust collectors, a mechnical atomization system,
and an exhaust gas discharge tower (Refer to Appendix I-L ).
46

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Initial start—up of the Recovery Boiler with fuel oil
occurred on December 30, 1974 but instrument problems
required a temporary shut-down of the operation (Sto].z,
letter of February 10, 1975). Interinittant operation
continued during the first two weeks of January 1975,
allowing the mill to adjust and calibrate the system’s
instruments (Stolz, letter of February 10, 1975).
The SSL firing first occurred on January 16, 1975 for
an eight hour period (Stolz, letter of February 10, 1975).
Between January 16 - February 2, 1975 the system operated
at a low rate on a part time basis (Stolz, letter of
February 10, 1975). Problems developed with the VRC
and the system was shut-down during February 1975.
Operation was resumed in March 1975; however problems
continued to plague the system (Stolz, letter of March 7,
1975)
On December 19, 1975, ITT Rayonier claimed they had
achieved all the requirements contained in Stipulation No.
9586 and requested the courts to dismiss the complaint
(Coate, letter of September 9, 1976). EPA required the
mill to demonstrate proof of their 85 percent recovery
and 312,000 lbs/day (141,523 kg/day) discharge limitation
of SSL solids. Analysis of the mill data based on a monthly
average (December 1975 - July 1916) indicated compliance
only 41 percent of the time (Coate, letter of September 9,
1976) (Table 1—10). As shown in Table 1—10 the increased
recovery of SSL solids generally decreases the amount of
BOD discharged.
By mid 1976 ITT Rayonier recognized that the installed
Recovery System was not capable of meeting the 85 percent
47

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Table 1-10. SSL & SOD DATA FOR ITT RAYONIER, INC.,
PORT ANGELES, WASHINGTON
Source: Coate, letter of September 9, 1976
SSL
BOD5
Average
Average
Average
Generated
Discharged
Recovery
Discharged
Date
lbs/day
lbs/day
%
lbs/day
12/75
997,000
161,000
84
——
1/76
1,232,000
370,000
70
329,000
2/76
1,270,000
194,000
85
216,000
3/76
1,284,000
318,000
75
200,000
4/76
1,312,000
354,000
73
264,000
5/76
1,222,000
555,000
55
346,000
6/76
1,280,000
134,000
90
214 , 000 a/
7/76
1,415,000
147,000
90
——
Average
1,252,000
279,000
78
262,000
Maximum
1,415,000
346,000
a! Data for 6/1 - 6/22
48

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SSL incineration requirement on a continous basis (Rogstad,
MER of June 4, 1976). The mill then composed a task force
to design the necessary modifications to allow the Recovery
System to achieve compliance (.MER June 4, 1976).
In J ly 1976 the mill requested a third modification of .ts
NPDES permit (No. WA 000079—5) to increase the average
discharge of SSL solids and BOD to 576,000 lbs/day (261,000
kg/day) and 412,000 lbs/day (186,688 kg/day), respectively
(Rogstad, letter of July 19, 1976; Rock, letter of August
16, 1976). EPA denied approval of the modifications
(Coate, letter of September 9, 1976).
ITT Rayonier submitted a proposed compliance schedule for
the SSL Recovery System to DOE indicating compliance as
of October 1, 1977 (Rogstad, letter of December 29, 1976).
On March 23, 1977, DOE issued a Regulatory Order Docket
( In re : Compliance by ITT Rayonier Inc., Port Angeles
with Chapter 90.48 RCW and the Rules and Regulations of
DOE, Docket No. DE 77—143 (DOE) Order filed March 22, 1977,
hereafter cited as DOE Docket DE 17—143) requiring the mill
to submit Quarterly Reports on the Progress of the Recovery
System to achieve compliance by October 1, 1977 (Rogstad,
letter of April 8, 1977).
A limited analysis of the data (July 1977 — July 1979
demonstrates the mill complied with its SSL solids discharge
limitations (15 percent of the total SSL solids and 312,000
lbs/day (141,523 kg/day) SSL solids) on several occasions;
however the mill has not proven satisfactory compliance with
Stipulation No. 9586 to warrant its dismissal ( United States
of A.merica v. ITT Rayonier, Inc . No. 9586 (W.D. Washington)
Reply to Memorandum in Support of the Government’s Motion
for Extension of Time to Respond to Defendant Dismissal
Motion filed July 24, 1980).
49

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2. Pernits and Regulations
In 1955 the State of Washington initiated a permit program
allowing the WPCC to require effluent standards for indus-
tries. ITT Rayonier was issued its first temporary state
discharge permit in 1956 (FWPCA 1970). A subsequent permit
was issued on a temporary basis on May 19, 1961 (Permit No.
T402) (FWPCA 1970). Conditions in this permit were pro-
tested by the mill and WPCC withdrew the permit and issued
Permit No. 1859 on December 18, 1962. This is the earliest
permit for ITT Rayonier, Port Angeles Division presently on
file with DOE, Lacey, Washington. The permit authorizes the
discharge of waste (defined as total volume of mill effluent)
to Port Angeles Harbor, not exceeding 35,500,000 gallons/day
(134,361,500 liters/day). The permit required some control
of settleable solids, in particular:
• barker effluents to be settled in an enlarged
mechnical clarifier
• various collection lines, sumps and pumps to re-
cover fiber from the machine room sewer system
• completion of the above facilities within 18
months of permit issuance
The permit indicated that a planned technical program
(maximum, 2 years) to determine the effects of SSL on the
receiving waters had been initiated by the WPCC. Based on
the results of this study and the exchange of data between
WPCC and the mill, WPCC would annually review the progress
of ITT Rayonier’s SSL program. The WPCC could require the
mill to take further corrective action regarding the dis-
posal of SSL; however the permit’s specific requirements
included:
• improvements to the SSL blowpit recovery system
• completion of these facilities within 18 months
of permit issuance.
50

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The permit required the monitoring data on specific
effluent characteristics to be submitted monthly (Dis-
charge Monitoring Reports (DMR)). Monitored effluents
included:
• Pulp production (tons)
• Waste flow for each outfall (gallons)
• SCS for each outfall (pounds)
• TS for each outfall (pounds)
Further conditions required:
• In—plant slime control programs and procedures
to be submitted to WPCC
• Sanitary sewage to be treated in sewage treat-
ment facilities on the mill site or divert the
sewage to a municipal sewage treatment plant
(STP)
chronologically, the next ITT Rayonier waste discharge
permit on file at DOE, Lacey, Washington was issued to
the mill on March 30, 1970 (Permit No. T-2867). This
permit required primary treatment and other waste control
facilities to be placed in operation between 1970 and 1974.
The main provisions were:
• discharges were not to exceed 36,280,000 gallons!
day (137,319,800 liters/day)
• a primary treatment facility be designed by June 1971
and completed by September 30, 1972 to remove all
settleable solids (permit condition I.A)
• that a minimum of 80 percent of the sulfite waste
liquor be removed previous to discharge into state
waters or the SSL discharges be limited to 3,700,000
pounds/day (167,832 kg/day) by June 30, 1974.
(permit condition I.B)
• that a submarine outfall be constructed, equipped
with a diffuser discharging to the deeper waters of
Port Angeles, and be placed in operation by June 30,
1974 (permit condition I.C)
• that existing sludge beds within a radius of 2000 feet
(610 m) of any mill outfall be removed by dredging
by December 31, 1973 (permit condition I.D)
51

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A new effluent characteristic was to be monitored and
included in the DMRs submitted to the WPCC. This para-
meter was BOD. The requirement for the in—plant slime
control program remained the same as in the previous per-
mit but sanitary sewage was required to be diverted to
the Port Angeles STP.
After issuance of Permit No. T—2867, ITT Rayonier sub-
mitted an application requestii ig the right to discharge
an additional 1,720,000 gallons/day (6,510,200 liters!
day). On June 29, 1970 the WPCC issued a revised dis-
charge permit (No. T-3373) for the additional waste; how-
ever the mill had to fully satisfy conditions l.A , I.B,
I.C, and I.D of Permit No. 2867 before WPCC would author-
ize discharge of the additional 1,720,000 gallons/day.
The remainder of Permit No. T-3373 resembled its pre-
decessor (No. T-2867).
ITT Rayonier appealed both Permit No. T-2867 and No.
T-3373 to the Pollution Control Hearings Board (PCHB)
and a final decision and order was determined by PCHB
on March 30, 1971 ( In re : ITT Rayonier, Inc., PCHB Docket
No. 70—2, PCHB Docket No. 70-3 (PCHB, State of Washington).
Final Decision and Order filed March 30, 1971). During
this same period, the United States Government filed a com-
plaint ( United States of America v. ITT Rayonier Inc Civil
Action No. 9586 (W.D. Washington) Complaint, filed March 30,
1971) against the mill alleging that ITT Rayonier had not
obtained a discharge permit from the Corps of Engineers
therefore violating Section 13 of the 1899 Refuse Act. As
a result of the complaint a Stipulation No. 9586 and Order
Granting Continuance ( United States of America v. ITT Rayon—
ier, Inc . Civil No. 9586 (W.D. Washington) Order Granting
Continuance filed April 9, 1971, hereafter cited as Order
9586) were entered in the federal courts.
52

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In summary, the stipulation specified that:
• ITT Rayortier construct a primary treatment
facility and have it operable by September 30,
1972
• all effluent streams in excess of 0.3 lbs (0 ,14 kg)
volatile suspended solids per 1000 gallons (3,800
liters) receive primary treatment.
• ITT Rayonier construct a submarine outfall and
have it operable by September 30, 1972. All mU].
residual wastes and no more than 15% of the total
SSL solids generated by the mill (14-day average)
were to be discharged through the submarine outfall
• ITT Rayonier remove by dredging the sludge beds
located adjacent to the mill by September 30, 1974
unless the EPA or State of Washington waives the
requirement
The stipulation required 85% recovery of SSL in contrast
to the 80% recovery originally required in Permit No. T-2867.
Following December 31, 1974 the discharge of SSL solids
was not to exceed an average of 15% of the total SSL solids
generated by the mill during a 14—day period. Further, the
SSL solids discharged by ITT Rayonier during a 14-day period
were limited to an average of 1,560 tons/day (3,120,000 lbs/
day) (1,415,232 kg/day) SSL based on 10% solids as measured by
the Pearl-Benson Index (PBI) test.
The Order Granting Continuance (No. 9586) ordered the stipu-
lation involving the complaint (Stipulation No. 9586) be contin-
ued until June 30, 1975 or until ITT Rayonier complied with
all the conditions. Until the Stipulation (No. 9586)
is dismissed by the courts, ITT Rayonier is required to
abide by both the conditions of the Stipulation and its
Waste Discharge Permit issued by DOE.
On August 30, 1974 DOE, successor to WPCC, issued National
Pollutant Discharge Elimination System (NPDES) Permit No.
WA 000079—5 to ITT Rayonier with an expiration date of
July 1, 1978. The permit required the mill:
53

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• to achieve specific Initial, Interim and Final
ef fluent limitations and monitor the levels
discharged (Table I-il)
• to construct facilities to achieve the Interim
effluent levels by December 1, 1974 and attain
compliance by April 1, 1975
• to construct facilities to achieve Final effluent
levels by March 1, 1977 and attain compliance
by July 1, 1977
• to discharge wastes that allow 100% survival of
any salmon test fish in 65% concentrated treated
mill effluent for 96 hours. Compliance with the
bioassay requirement was to be achieved by July 1,
1977
• to submit a Spill Prevention, Containment and
Countermeasure Plan
• to confine temperature increases of the receiving
waters to the mixing zone in the vicinity of
outfall 007. No measurable temperature increase
(0.50 F) above natural conditions was allowed to
occur outside the mixing zone.
• to devise a plan by March 1, 1975 for handling all
of the solid waste generated by the mill
• to report annually to DOE the mill’s in-plant
slime control program and procedures to discharge
all sanitary sewage to Port Angeles STP
• to eliminate visible discharge of foam to the
receiving waters after March 1, 1975
In October 1974 ITT Rayonier appealed to the PCHB the condi-
tions pertaining to pH and toxicity as contained in the NPDES
permit issued August 30, 1974; however the mill agreed to the
remaining permit requirements which included construction of
secondary treatment (DOE 1977). The appeal lead to an
Amended stipulation and Agreed Order between the mill and
DOE on February 10, 1975 ( In re : NPDES Permit No. WA 000079—5
ITT Rayonier, Inc. v. DOE, PCHB 712 mended Stipulation and
Agreed Order (PCHB Washington) filed February 10, 1975).
The PCHB remanded the NPDES Permit to DOE and ordered the
permit to incorporate the following changes indicated in the
stipulation:
54

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• In regard to the final effluent limitations 1
(footnote f, page 5):
“The biochemical oxygen demand, suspended solids
and H limitations will be modified to be consis-
tent with the applicable final effluent guidelines
when promulgated by EPA in the Federal Register ,
or as thereafter modified by final action conse-
quent upon any appeal from such guidelines.”
• Condition S7a shall read:
Perinittee shall monitor composite waste discharge
with respect to toxicity to salmonid species.
Cl) The monitoring shall be conducted in accordance
with a program developed by the permittee in
consultation with the Department and submitted
for approval by April 30, 1975.
(2) Such program shall commence by July 1, 1975.
The results thereof shall be reported every
six months beginning January 1, 1976.
(3) A final report shall be submitted by April 30,
1978, detailing monitoring results of various
concentrations of treated effluent. Such report
shall include evaluation of measures necessary,
if any, to prevent toxicity to sa].monid fishes
in a 65% concentration of industrial wastewater
f or a 96—hour period.
ITT Rayonier’s first NPDES Permit (No. WA. 000079-5) was mod-
ified on three additional occasions (January 24, 1975,
October 22, 1975, and March 1, 1977). Due to strikes, equip—
znent deliveries and start-up problems the following modifica-
tion to the permit were made on January 24, 1975 (Behike,
letter of Jai .uary 24, 1975):
• Initial effluent limits were to be effective until
May 31, 1975 (Table I—li)
• Interim effluent limits were to be effective as of
June 1, 1975 (Table I—li)
• Construct facilities to achieve Interim effluent
limits by January 31, 1975 and achieve comparable
compliance by May 31, 1975
Operational problems with the newly installed Recovery
System (December 1975) and a 73 day Western Pulp and Paper
55

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Table I-li. HISTORY OF MODIFICATIONS TO NPDES PERMIT NO. WA 000079-5
ISSUED TO ITT RAYONIER, INC., PORT ANGELES, WASHINGTON
S.1 INITIAL EFFLUENT LIMITS (IN THOUSANDS)
Parameter Original Requirements Permit Modifications
Daily Daily Date Date Daily Daily Date
Average Maximum Effective Modified Average Maximum Effective
BOD (5 day) 590.0 690.0 8/30/74— 1/24/75 N/M N/M 8/30/74—
lb/day 3/31/75 5/31/75
10/22/75 N/M N/M 8/30/74-
11/30/75
SCS 14.0 24.0 8/30/74— 1/24/75 N/N N/N 8/30/74—
lb/day 3/31/75 5/31/75
10/22/75 N/M N/M 8/30/74-
11/30/75
Footnotes Original Requirement Permit Modification
Date Date Date
Comment Effective Modified Comment Effective
f Did not exist N/A 10/22/75 “After 9/1/75 and con- 8/30/74—
tinuing throqgh 11/30/ 5/31/75
75 all unburned SWL
will be intercepted to
the storage lagoon for
storage and reintroduc-
tion to the chemical
recovery facility to the
maximum extent possible,
prior to discharge to the
receiving waters.”
(Permit No. Wa 000079-5)
N/M - No modification _____________________________

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Table I—lj,Page 2
S.,2 INTERIM EFFLUENT LIMITATIONS (IN THOUSANDS) (a)
Parameter Original Requirements Permit Modifications
Daily Daily Date Date Daily Daily Date
Average Maximum Effective Modified Average Maximum Effective
BOD (5 day) 300.0 400.0 5/1/75 — 1/24/75 N/M N/M 6/1/75 -
lb/day 7/1/77 7/1/77
10/22/75 N/M N/M 12/1/75-
7/1/77
SCS 11.0 20,0 5/1/77 — 1/24/75 N/M N/M 6/1/75 —
lb/day 7/1/77 7/1/77
10/22/75 N/M N/M 12/1/75-
7/1/7 7
SSL solids 247.0 N/R 5/1/77 - 1/22/75 N/M N/M 6/1/75 -
lb/day 7/1/77 7/1/77
10/22/75 N/M N/M 12/1/75-
7/1/77
N/R - No Requirement
(a)The mill was required to abide with these limits and those requirements contained
in Stipulation No. 9586, whichever was more restrictive.

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Table I-U,Page 3
S.3 FINAL EFFLUENT LIMITATIONS (IN THOUSANDS)
Parameter Original Requirements Permit Modifications
Daily Daily Date Date Daily Daily Date
Average Maximum Effective Modified Average Maximum Effective
BOD (5 day) 39.0 59.0 7/11/77 — 3/1/77 29.0 55.0 7/1/77 —
lb/day 7/1/78 7/1/78
mid 1978 N/H N/M 7/1/77 -
8/2 9/7 9
TSS 13.0 26.0 7/1/77 — 3/1/77 41.0 77.0 7/1/77 —
lb/day 7/1/78 7/1/78
mid 1978 N/M N/H 7/1/77 -
8/29/7 9
pH 6.0(b) 9.0 7/1/77 — 3/1/77 5.0(b) N/M 7/1/77
7/1/78 7/1/78
mid 1978 N/ I l N/M 7/1/77 -
8/29/79
Footnotes Original Requirement Permit Modification
Comment
Comment
Date Date
Effective Modified
f The biochemical oxygen 7/1/77 1975(c)
and suspend d solias 4i—
mitations will be modi-
fied to be consistent
with the applicable final
effluent guidelines when
oromuloated by EPA in the
Federal Registηr, or as
thereafter modified by
final action consequent
up n any appeal from such
guidelines.
mid 1978
(b)mjnjmum pH
(c)permit remanded to DOE on February 10, 1975 (PCHB 712)
permit but no specific modification data was indicated
Date
Effective
7/1/77 —
7/1/78
The biochemical oxygen
demand, total suspηnded
solids 1 and pH limita-
tions will be modified
to be consistent with
tI applica1 1e final
effluent guidelines when
promulgated by EPA in the
Federal Registηr 1 or as
thereafter modified by
final action consequent
upon any appeal from such
guidelines.
N/M 7/1/77 —
/29/79
to incorporate this change in the
in the permit.

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Workers strike lead to a second modification of the permit
(Rogstad, letter of July 23, 1975). The EPA approved the
following October 22, 1975 modifications to NPDES Permit
No. WA 000079—5 (Coate, letter of October 15, 1975):
• Initial effluent limits for discharge 007 were
to be effective until November 30, 1975
• Interim effluent limits were to be effective as
of December 1, 1975
• From September 2, 1975 until November 30, 1975
all unburned SSL was to be diverted to the SSL
storage lagoon, stored and returned to the Chem-
ical Recovery System “... to the maximum extent
possible prior to discharge to receiving waters.”
• Facilities to achieve Interim effluent limits were
to be in compliance by December 1, 1975
As a result of footnote (f) CTable I—il) contained in the
mill’s NPDES permit, ITT Rayonier concluded that neither the
Final effluent limits, nor the compliance schedule for
secondary waste abatement facilities were effective until
the final effluent guidelines for dissolving grade sulfite pulp
mills were promulgated by EPA and allowed to receive judicial re-
view. When the mill did not submit their required final plans for
secondary treatment facilities to obtain DOE’S approval by October
1, 1975, DOE issued an Order ( In re : Compliance by ITT Rayonier,
Port Angeles with Chapter 90.48 RCW and Regulations of DOE,
Docket No. DE 75—226 (DOE) order filed December 31, 1975)
requiring ITT Rayonier to submit such plans. ITT Rayonier
appealed this matter to the PCHB ( In re : Compliance by ITT
Rayonier, Port Angeles with Chapter 90.48 RCW and the Regula-
tions of DOE PCHB No. 970 (PCHB, Washington) Notice of
Appeal From and Application for Stay of DOE order dated
December 31, 1975 (Docket No. DE 75-226) filed January 29,
1976). Also, on February 27, 1976 the mill filed applications
with DOE to modify or stay the compliance schedule “...until
completion of judicial review of EPA’S effluent limitations
guidelines relating to dissolving grade sulfite pulp mills,”
59

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(In re: ITT Rayonier, Inc., Port Angeles Division, NPDES
Permit NO. WA 000079—5 (DOE) Docket No. DE 76—26, Order
Denying Applications for Modifications and Stay filed
March 17, 1976; hereafter cited as Docket No. DE 76—26).
This request was denied by DOE on May 17, 1976 (Docket
No. DE 76-26). The mill appealed to the PCHB (PCHB No. 1025)
Additionally, on February 27, 1976 ITT Rayonier filed an
application with DOE to stay the effectiveness of DOE’s
Order Docket No. 75—226. This application was denied by
DOE on May 19, 1976 ( In re : ITT Rayonier, Inc., Port
Angeles Mill, NPDES Permit No. WA 000079-5 (DOE) Docket No.
DE 75—226, Order Denying Application for Stay filed May 19,
1976). ITT Rayonier appealed the denial to the PCHB
(PCHB No. 1042). Until a final order was issued regarding
PCHB No.s 970 and 1025, the PCHB ordered a stay on the filing
of final plans by ITT Rayonier (Docket No. DE 75-226) ( In re:
ITT Ravonier, Inc. v. State of Washington , PCHB No.s 970,
1042 (PCHB) Order of Stay filed July 21, 1976). On November
5, 1976 the Final Findings of Fact on PCHB No.5 970 and 1025
affirmed both of the DOE decisions regarding Dockets
DE 75—226 and DE 76-26 C In re: ITT Ray’onter, Inc. v. State
of Washington , PCHB NOSS 970 and 1025 (PCHB) Final Findings
of Fact, Conclusion of Law and Order filed November 5, 1976).
The PCHB also remanded NPDES permit No. WA 000079—5 to DOE
with the following instructions:
“...to replace the effluent limitations subject to
footnote f/, first, by limitations consistent with
app1icab1 EPA Guidelines as promulgated in the
Federal Register and, thereafter, by limitations
consistent with such Guidelines as modified by final
action consequent upon any appeal from such guide-
lines.”
These modifications for the final effluent limitations were
approved by DOE by February 14, 1977 to modify the NPDES per-
mit on March 1, 1977 (Table I—li). (Provost, letter of February
14, 1977)
60

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ITT Rayonier appealed PCHB’s final decision on No.’s 970 and
1025 to the Superior Court of Clallam County. On May 10,
1977, the Court reversed the previous PCHB decision ( In re :
ITT Rayonier, NPDES Permit Application No. WA-000079—5 (EPA)
Public Hearing to Consider Objections to Issuance of Permit
filed March 26, 1980; hereafter cited as Public Hearing,
March 26, 1980). At this time DOE appealed to the State
Supreme Court and in 1978 the court upheld the decision of the
Superior Court of Clallam County ( ITT Rayonier v. State of
Washington , No. 44957 (Washington State Supreme Court), here—
after cited as No. 44957).
According to the court, footnote f contained in ITT Rayonier’s
NPDES Permit (No. WA 000079—5) allowed the mill to complete
its appeal of EPA’S effluent limitation guidelines for dis-
solving grade sulfite mills before the permit effluent limits
(S.3) would be final. As a result the court postponed the
permit compliance schedule until the EPA effluent guide-
lines were judicially settled. Following the reinstate-
ment of the compliance schedule by DOE, the mill would be
allowed a minimum of 3 months before being required to sub-
mit final construction plans.
The final effluent guidelines for dissolving grade sulfite
mills were promulgated by EPA on January 6, 1977. Several
industries challenged the limitations and on September 5,
1978 the U.S. Court of Appeals for the District of Colum-
bia Circuit remanded to EPA the BOD limitations for acetate
grade dissolving sulfite mills (In_re: ITT Rayonier, NPDES
Permit Application No. WA 000079-5 (EPA) Public Hearing to
Consider Objections to Issuance of Permit filed March 26,
1980, hereafter cited as Public Hearing, March 26, 1980).
In 1977 EPA issued a Notice of Violation to ITT Rayonier
and the State of Washington ( In re : NPDES Permit No. WA
000079—5 for ITT Rayonier, Inc. No. X76—12—08—30l (U.S.E.P.A.)
Notice of Violation filed March 30, 1971). The violation
found that ITT Rayonier had not complied with the construc-
61

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found that ITT Rayonier had not complied with the construc-
tion and waste abatement schedule designated in its NPDES
Permit No. WA 000079—5. As a result the mill would not be
able to achieve the final BOD effluent limitations by
July 1, 1977. To enforce these permit conditions the fed-
eral government filed a complaint in the U.S. Western Dis-
trict Court of Washington (C77-289M) which lead to an Order
Granting Motion for Partial Suxnmary Judgement (Order No.
C77-289M). ITT Rayonier was ordered to achieve the final
effluent limitations contained in NPDES Permit No. WA
000079-5 by June 5, 1979; however this decision was reversed on
September 15, 1980 by the United States 9th Circuit Court of
Appeals (No. 77—3672).
By April 1978, ITT Rayonier filed an application for exten-
sion on its NPDES permit expiration date from July 1, 1978
to August 29, 1979 (DOE 1978), which was approved by DOE
by mid 1978 (Rock, letter of April 28, 1978). ITT Rayonier
applied for a new NPDES permit on February 27, 1979 (Public
Hearing, March 26, 1980). On April 23, 1979 a proposed
permit based on the conclusions of the State Supreme Court
decision (No. 44957) was forwarded to EPA (Provost, letter
of April 23, 1979). The proposed permit did not contain the
Best Practical Control Technology (EPT) limits (Dissolving
grade Sulfite Mills) for BOD; therefore EPA objected to the
issuance of the permit (Reed, letter of July 20, 1979).
ITT Rayonier opposed EPA’s objection ( In re : ITT Rayonier
NPDES Permit application No. WA 000079—5 (EPA) Public Hear-
ing to Consider Objections to Issuance of Permit, March 26,
1980). ITT Rayonier was required to comply with its ex-
pired NPDES Permit NO. WA 000079-5 until a new permit was
issued.
On September 12, 1980, ITT Rayonier was issued a new NPDES
Permit (No. WA 000079—5) by EPA (Dagelen, personal communi-
cation of October 1, 19801. The mill accepted the designated
BOD limits (average 30,000 lbs/day; 13,608 kg/day and maxi-
mum 57,000 lbs/day; 25,855 kg/day) but contested the total
suspended solids limitations (Waite, personal communication
of November 25, 1980).
62

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3. Compliance History
Permit requirements prior to 1970 are vague and contain
references to “improvements” to various systems as well as
certain technical studies to be undertaken by ITT Rayonier.
Correspondence during this period is practically non—existent
in the available files; therefore discussions of compliance
with installation and operation of required facilities
will begin with 1970. Violations of the NPDES permit
effluent limitations and overflows/spills recorded by ITT
Rayonier are summarized from 1975 to mid 1980, unless indi-
cated differently (Refer to Table 1—12 and Appendix I—M for
further information on these violations).
During 1970 ITT Rayonier was actively discharging residual
mill waste through a minimum of 5 outfalls (see applicable
DMR’s, 1970). The mill had obtained neither an outfall per-
mit nor a discharge permit from the Corps of Engineers in
accordance with Section 10 and Section 13 of the Rivers and
Harbors Act of 1899, respectively (FWPCA 1970). In March 1971
filing Complaint No. 9586, the United States of America alleged
ITT Rayonier had violated Section 13 of the 1899 Rivers and
Harbors Act (Complaint No. 9685). The resulting Stipulation
(No. 9586) required specific provisions which resembled those
in the previously appealed permit (No. T-2867). An Order
of Continuance accompanied the Stipulation (No. 9586) indi-
cating the requirements of the Stipulation would be continued
until June 30, 1975 or until ITT Rayonier complied with all
the conditions contained in the Stipulation. As of Novem-
ber 1980 the courts have not dismissed Stipulation 9586;
therefore ITT Rayonier is required to abide by both the Stip-
ulation and its current NPDES Waste Discharge Permit.
ITT Rayonier did comply with the requirement for in-
stallation and operation of primary treatment facilities and
63

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Table 1-12. SUMMARY OF VIOLATIONS RECORDED BY ITT RAYONIER, INC.,
PORT ANGELES, WASHINGTON
Time Daily Average Daily Maximum Total
Period Parameter Violations Violations Violations
1/75 - Overflows! N/A N/A 566*
6/80 Spills
7/77 - SSL solids N/A N/A 152
7/79 ( 15%)
1/75 — BOD 35 609* 644
6/80
1/75 — SCS 14 171 185
6/80
7/77—6/78 TSS 8 45 53
3/7 9—6/8 0
7/77—6/78 pH 490** 2 492
3/7 9—6/80
N/A - Not Applicable
* Violations not recorded on a daily basis in the appropriate tables
(Appendix I-M) were only counted as one violation even though the
incident was indicated as N/A, continuous, intermittent etc.
** Daily minimum violations
64

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a submerged outfall by September 30, 1972. Also at this
time all residual mill wastes and no more than 15% of the
mill’s generated SSL solids were to be diverted to the sub-
merged outfall (007) (Stipulation No. 9586). The unincin—
erated SSL solids were to be discharged through 003A until
the Recovery Facilities caine on line December 31, 1974
(Bodien, personal communication of September 4, 1980).
Wastes from 5 minor drains (containing residual mill wastes
and cooling waters) were not diverted to the submerged out-
fall until late 1972 or early 1973 (Hawks, letter of Sept-
ember 17, 1972; Hawks, letter of December 7, 1972 and Mile—
man 1972)
Despite the rerouting of all residual waste streams except
003A to the submerged outfall , by early 1973 numerous
unauthorized discharges to the Harbor have continued to occur
through non-permitted point sources (Table I—M—1). The major-
ity of these are a result of pump failures in surnps that are
to divert the effluent to the primary clarifier or submerged
outfall.
Previous to July 1978 the minor intermittent overflows occur-
ring at the mill were not always reported to DOE (Hawks,
letterof June 20, 1978). Beginning July 1978 DOE requested
the mill to continue reporting major overflows anJ begin
to report minor overflows (Primary Treatment System Overflow
Log, PTSOL) and include the PTSOL as an attachment to the
monthly submitted DMR’s (Hawks, letter of July 5, 1978). The
earliest available PTSOL occurs in March 1979. As a result
the data in Table I-M—l previous to March 1979 represents the
major overflows and spills committed by the mill; therefore
a tabulation of these violations indicates a minimum incident
count of overflows occurring at ITT Rayonier from January
1975 to June 1980 (Table I— 12).
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Recovery facilities were not installed and operable by the
required December 31, 1974 date (Stipulation No. 9586).
Despite the fact NPDES Permit No. WA 000079—5 issued August
30, 1974 had been modified to require operation of the
facility by December 1, 1975, the Stipulation (No. 9586)
has not been dismissed by the courts. Operation of the
Recovery Facilities was scheduled by DOE and the mill to be
attained by October 1977 (Rogstad, letter of April 8, 1977,
DOE Docket DE 77-143).
An analysis of the available SSL solids generated and dis-
charged by the mill (June 1977 — July 1979) indicates that
the 15% SSL discharge obtained during a 14-day period was
violated during various times of every month from August
1977 — February 1978 (Table I—M—2). Beginning July 31, 1978
to January 10, 1979 the mill violated their SSL provisions
on 22 occasions (Table I—M—2). From June 1977 to July 1979
the mill discharged more than 15% of the total SSL solids
generated by the mill (14—day average) on 152 occasions
(Table 1—12) which indicates malfunctions in its Recovery
facilities. The sporadic operation of the Recovery Boiler
from January 1975 to January 1979 provided in available corres-
pondence and analysis of the 14—day moving average (Section
I.C.]. Chemical Recovery and Table I-M—2) indicates a viola-
tion for a minimum of 4 years of the mill’s permit and Stip-
ulation No. 9586 requirement for an operable Recovery Boiler
(December 31, 1974).
The only extensive available daily record of SSL spills
occurring at the mill was provided in the Daily Environmental
Reports (DER) for 1978. SSL spilled from the Evaporator
Feeder, intermediate SSL storage area, unfiltered SSL storage
area, and Heavy Liquor Tanks A, B and C on various occasions
during six months of the year (January — April, June, and
August). It is unclear if these spills were diverted to
outfall 007 (now 001) or were discharged through an authorized
discharge point. If the spills were diverted to 007
66

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(now 001) and caused a 14-day moving average of discharged
SSL solids in excess of 15% of the total generated by the
mill (or 312,000 lbs/day) (141,523 kg/day) the violation
would be indicated in Table I-M-2.
Any SSL spills known to be a discharge from an unauthorized
point source are represented in Table I—M-l. From January
1975 to June 1980 two SSL leaks to the Bay (May 10, 1976 and
June 1977) were recorded in the available information. Since
the mill did not have secondary treatment facilities operable
by the July 1, 1977 date as contained in the final limitations
of the NPDES permit, DOE continued to require the mill, to meet
their interim permit limits. This included the SCS parameter.
As indicated in Tables I-M—5 and I-M—6, the violations of
SCS after July 1, 1977 were assessed by DOE; however EPA held
ITT Rayonier to the TSS requirements in the Final limits of
the NPDES permit. By not including the TSS results in their
DMR’s from July 1, 1977 to September 1979 ITT Rayonier vio—
lated a permit requirement. Subsequent to secondary treat-
ment installation (October 12, 1979) the mill exceeded their
TSS daily average six months and the daily maximum on 35
occasions (Tables 1—17, I—M—7 and I—M—8).
The permitted average and maximum BOD limits were violated
almost constantly from July 1977 to September 1979
(Tables I-M-3, I-M—4). Even after the installation of second-
ary treatment facilities the mill violated the 29,000 lbs/day
(13,154 kg/day) BOD average limit during 6 months (Table I-M-3).
The maximum limit during this 6 month period (November 1978 -
June 1980) was exceeded on at least 6 occasions (Table I-M—4).
The pH limits were first required in the mill’s NPDES permit
as of July 1, 1977. The effluent from 007 was required to
range from 5.0 to 9.0 on a daily basis. The DMR’s
did not include pH until October 1979, but the mill, recorded
effluent pH in their Submerged Outfall Characteristic (SOC)
67

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reports. From July 1977 to June 1980 the mill violated their
minimum limit (5.0) on 490 occasions (Tables 1—12, I—M—9).
From July 1978 to February 1979 there was no available daily
information (SOC); therefore these violations may represent
a minimum count. The maximum pH limit was violated on two
occasions (May 24 and 26, 1980) (Table I—M—1O).
68

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REFE RENCES
CHAPTER I
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Aspitarte, T.R. and B.C. Smale. March 13,1972. Sludge Bed
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70

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Cameron, Bruce A. August 31, 1977. Notice of Penalty Incurred
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Dagelen, Bonnie. October 1, 1980. Personal Communication
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of Technical Services, DOE.
72

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Hawks, Frank C. August 25, 19.72, Letter to John B. Gray.
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EPA, Region X, Seattle, Washington.
ITT Rayonier, Inc. October 6, 1976. Quarterly Review . ITT
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Flow. (Drawing initialed by DSR). ITT Rayonier, Inc.,
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DOE, Olympia, Washington.
73

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Knudson, James C. December 9, 1971. Letter to Crown
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Monthly Environmental Summary. March - July, October 1976,
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Permit No. T-402. May 19, 1961. Waste Discharge Permit
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Provost, Donald 0. February 14, 1977. Letter to Lyman J.
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Submerged Outfall Characteristics Reports. January, February,
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Pollutional Effects of Pulp and Paper Mill Wastes in
Puget Sound . Washington State Enforcement Project. 474pp.
United States Environmental Protection Agency. December 1974.
Evaluation of ITT Rayonier, Inc. Outfall, Port Angeles
Harbor, Washington . National Field Investigations Center.
Denver, Colorado. 100 pp.
Ventron Industries. No Date. Brochure. Ventron’s process
with the Boral solution.
Vogt, Craig and Richard Kinch. December 1976. Development
Document for Effluent Limitations Guidelines (Best Practical
Control Technol gy Currently Available) for the Bleached
Kraft, Groundwood, Sulfite, Soda, Deink, and Non-Integrated
Paper Mills Segment of the Pulp, Paper and Paperboard Mills
Point Source Category . Effluent Guidelines Division Office
of Water and Hazardous Materials, EPA. Washington, D.C. 638 pp.
Waite, T. November 25, 1980. Personal Communication to
Kathryn Pazera, Biologist, NEC. Seattle, Washington.
79

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Walters, R. January 24, 1972. Letter to J.G. Gray, Resident
Manager, ITT Rayonier, Inc. Port Angeles, Washington.
Washington State Department of Ecology. 1974. Technical
Information on Crown Zellerbach Corp., Port Angeles,
Washington. DOE. Lacey, Washington.
Washington State Department of Ecology. March 4, 1977.
ITT Rayonier, Inc. at Port Angeles, Comments.
Washington State Department of Ecology. April 28, 1978.
Announcement of Proposed Amendment for National Pollution
Discharge Elimination System (NPDES) Permit to Discharge
to State Waters. Olympia, Washington.
Washington State Department of Ecology. May 1978. Final
Environmental Impact Statement. Proposed Secondary
Wastewater Treatment Facility at ITT Rayonier, Inc., Port
Angeles, Washington . This incorporates the Draft
Environmental Impact Statement issued March 1978.
Washington State Department of Ecology. February 1979. Final
Supplemental Environmental Impact Statement. Proposed
Construction and Operation of Sludge Dewatering Equipment
and Temporary Landfill Disposal, ITT Rayonier, Inc., Port
Angeles, Washington . Final Supplement to May 1978 EIS.
Washington State Department of Ecology. No Date. Water Pollution
Abatement and Water Quality Improvement in Port Angeles
Harbor . DOE. Olympia, Washington.
Washington State Water Pollution Control Commission. May 13,
1970. Interim Policy Concerning Industrial Discharges of
Heavy Metals. Olympia, Washington.
Washington State Water Pollution Control Commission, U.S. Public
Health Service, and Fibreboard, Inc. April 1964 (a). In-
plant Survey, Fibreboard Paper Products Corporation.
Olympia, Washington.
Washington State Water Pollution Control Commission. U.S. Public
Health Service, and Fibreboard, Inc. October 1964(b). 1n
plant Survey, Fobreboard Paper Products Corporation.
Olympia, Washington.
Yake, B. February 14, 1980. Letter to Fred Fenske and Roger
Stanley.
Young, S.R. June 28, 1976. Letter to James C. Knudson, DOE.
Olympia, Washington.
80

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II. INDUSTRIAL AND MUNICIPAL EFFLUENTS AND COMPOSITION
This chapter presents an overview of effluents introduced into
Port Angeles Harbor (hereafter Harbor) and the adjacent Strait
of Juan de Fuca (hereafter Strait) from pulpmills and other
industrial and municipal, point source dischargers. The discus-
sion is based on historical records extending back to 1966,
before which there is little data. Subsection A contains a
description of effluent amounts from each discharger and his-
torical levels of monitored pollutants from the Crown Zeller-
bach, Fibreboard and ITT Rayonier pulpmills including biological
oxygen demand (BOD), suspended combustible solids (SCS), total
suspended solids (TSS), total solids (TS) and others. Sub-
section B provides a summary of time—periods when the mills were
not discharging effluents due to routine or nonroutine shutdown.
Subsection C discusses biologically toxic components of pulpmill
effluents, first in a general sense and then as applied to the
two presently operating Port Angeles pulpmills.
A. EFFLUENT DISCRARGERS
The receiving waters of the study area are divided into Class
A (Port Angeles Harbor) and Class AA (Strait of Juan de Fuca)
waters (Figure 11—1). The water quality criteria and standards
for these classifications are discussed in Section IV.A. Uti-
lizing available data on file with Washington State Depart-
ment of Ecology (DOE)—Southwest Regional Office, Olympia,
Washington; DOE - Lacey, Washington and U.S. Environmental
Protection Agency (EPA) — Region X, Seattle, Washington, an
inventory of discharges to the study area includes facilities
discharging directly to the receiving waters and those point
sources discharging into tributaries flowing into the Harbor and
Strait from the Elwha River east to the Dungeness River. The
direct receiving waters for each discharging facility are
indicated in Table 11-1, Figures 11-2, and 11-3, but the Harbor
and Strait are considered to be the final receiving waters.
81

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124”27
12f26 12f25 12 T24 12123
12i’22 12 f21 12 2O
Strait of Juan de Fuca
0
1
mU.s
Port AngeI.s Harbor
48’O
AA
rd
48O
48O
( Figure li-i. WASHINGTON STATE DEPARTMENT OF ECOLOGY WATER CLASS IFICATIONS
AT PORT. ANGELES, WASHINGTON
Source: DOE 1978 _____- __________________
)

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Table 11-1. KNOWN SURFACE WATER AND GROUND DISCHARGE
SOURCES IN THE PORT ANGELES AREA
(Refer to Figures 11—2 and 11—3)
Principal
Discharge
Type
oil
wastewater
Industrial
wastewater
Freshwater
Surface runoff
Industrial
wastewater
Fish rearing
was tewater
Industrial
wastewater
Domestic
Industril
wastewater
Non—contact
cooling water
Industrial
wastewate r/
Non —contact
cooling water
Map
Key
Facilities
Began
Discharge
Ceased
Discharge
1
Atlantic Richfield Co.
(ARCO)
1952
November
1976
2
Crown Zellerbach Corp.
1917
N/A
3
Dungeness Salmon Hatchery
reconstructed
1902
1974
N/A
4
Dungeness Oyster Farm
1974 (a)
N/A
5
Elwha Salmon Channel
1975
N/A
6
Fibreboard Paper Products
1917
November
1970
7
Heart 0’ the Hills
Campground
late
1960’s
N/A
8
ITT Rayonier, Inc.
1930
N/A
9
M & R Timber, Inc.
1958(b)
N/A
10
Peninsula Plywood Corp.
1941(b)
N/A
Receiving Waters
Previous Present
Tumwater N/A
Creek Closed
Straits/Harbor Straits
Harbor Harbor
Straits Straits
Elwha River Elwha River
Harbor N/A
Ennis Creek Ennis Creek
Harbor Straits
and/or Straits
Harbor Harbor
Harbor N/A
Harbor Harbor

-------
Table II-]. continued
Map
Began
Ceased
Principal
Discharge
Receiving
Waters
Key
Facilities
Discharge
Discharge
Type
Previous
Present
11
Port Angeles Car
Wash
1972
1977
Industrial
wastewater
Harbor
N/A
12
Port Angeles STP
1969
N/A
Municipal
Harbor(c)
Harbor(c)
13
Pres-Sure—Matic,
Inc.
1974(a)
N/A
Industrial
wastewater
Tumwater
Creek
Ground
14
U.s. Coast Guard
Air
1970
N/A
Oil
Harbor
Harbor
Station
wastewater
Source: Available applications, permits and correspondence for each industry on file
at DOE, Southwest Regional Office, Olympia, Washington and EPA, Region X,
Seattle, Washington.
(a) Earliest permit and/or application on file
(b) Date the most recent discharging source began operation
(c) The permit indicates receiving waters as the Straits but the discharge location is
in the Harbor.

-------
,_Discharge Figure II-Z. LOCATIONS OF
FacU lties (1966 - MID
C KEY:
THE
1980)
KNOWN DISCHARGING FACILITIES
IN THE PORT ANGELES AREA

-------
Strait of Juan de Fuca
•
L
*
U&R Tlflibsr
KEY:
Crown £.IISrbch
• Figure 11-3. LOCATION
* CHARGING
OF
TO
KNOWN
PORT
OUTFALLS DIS
ANGELES HARBOR J
les Harbor

-------
In addition to discharging facilities, the Harbor and Strait
also receive runoff from wood waste fills, log yards, and
the Port Angeles landfill (Figure 11—4).
During the past fifteen years (1966 — mid 1980), the Harbor
and adjacent waters of the Strait have been the receiving
waters for up to fourteen individual discharging facilities
(Figure 11—2). Presently ten facilities continue to discharge
treated wastes to the receiving waters with an additional 23
wood waste fills, log yards or landfills and one industry (PEe—
Sure—Matic, Inc.) contributing leachate to the ground or
adjacent tributaries (Table 11—1, Figure 11-2 and 11—4).
The major type of processed or treated effluent currently
released to the Harbor includes pulp and paper mill waste, domes-
tic or municipal sewage, oily waste water and non—contact
cooling water.
The sulfite (ITT Rayonier) and therrnomechanical (Crown Zeller-
bach) pulp and paper industry, salmon rearing facilities
(Elwha Rearing Channel and Dungeness Hatchery), and municipal
facility (Port Angeles Sewage Treatment Plant (STP)) contribute
the greatest waste flows to the study area with ITT Rayonier as
the leading discharger (Table 11-2). Prior to 1969, the start-
up date for the Port Angeles STP, available data indicates
ITT Rayonier, Crown Zellerbach and Fibreboard (closed in 1970)
were the major waste contributors to the receiving waters
(Table 11—2). From 1966 to 1970 the three pulp mills contri-
buted a daily combined average flow of 45.90 million gallons
per day (mgd) (173.7 million liters per day (mid)) (Table 11—2,
Figure 11-5). Despite Fibreboard’s closure, ITT Rayonier and
Crown Zelierbach averaged a combined flow of 45.96 mgd (174.0
mid) during 1971 to mid 1980 (Table 11—2, Figure 11—5).
87

-------
f KEY:
• Wood Waste Fills Figure 11-4. LOCATIONS OF THE KNOWN WOODWASTE FILLS, LOG-
Log Yards YARDS AND LANDFILLS IN PORT ANGELES, WASHINGTON
Source: Wood, personal communication of
August 11, 1980

-------
Table 11-2. AVERAGE ANNUAL DISCHARGES OF WASTE TO THE
PORT ANGELES AREA (mgd) 1966 - mid 1980
WASTE SOURCE 1966 1967 1968 1969 1970 1971 1972
Atlantic Richfield Co. (ARCO) HID HID N/D N/D N/D <.0001(a) <.0001(a)
Crown Zellerbach Corp. 9.15 7.71 8.34 7.98 6.25 7.43 1L35(b)
Dungeness Salmon Hatchery N/D HID HID N/D N/D HID N/D
Elwha Salmon Channel N/A N/A N/A N/A N/A N/A N/A
Fibreboard Paper Products Corp. 3.81 3.16 3.07 3.59 3.99 closed N/A
Heart 0’ the Hills Campground H/D HiD H/D N/D HID N/D N/D
I T T Rayonier, Inc. 34.08 33.23 35.70 35.73 33.72 33.25 32.26
M & R Timber, Inc. H/D N/D N/D HID N/D H/D H/D
Peninsula Plywood Corp. .002(c) N/D .17(e) .17(e) .17(e) .17(e) .17(e)
Port Angeles Car Wash N/D H/D N/D N/D H/D N/D N/D
Port Angeles STP N/A N/A N/A 1.70(c) 3.08 2.56 2.52
Pres-Sure-Matic, Inc. N/D N/D H/D N/D N/D HID H/D
U.S. Coast Guard Air Station N/D H/D H/D H/D N/D H/D H/D

-------
Table 11-2. Continued
WASTE SOURCE 1973 1974 1975 1976 1977 1978 1979 1980
<.0001(a)
11.48(b)
N/D
N/A
N/A
N/D
32.52
N/D
.17(e)
N/D
2.51
N/D
N/D
<.0001(a)
11.12(b)
N/D
N/A
N/A
N/D
34.33
.070(a)
.17(e)
N/D
2.52
N/D
<.0001(d)
N/A
10.88
15.00(d)
32.00(d)
N/A
.006
41.24
.077(e)
.090(e)
N/D
2.19
.0015(e)
<.0001(d)
N/A
8.41
15.00(d)
32.00(d)
N/A
.003
34.96
.077(e)
.090(e)
N/D
1.82
.0015(e)
<.0001(d)
N/D - no data available
N/A - not applicable
(a) Average daily flow indicated in available application
(b) Averages obtained from Primary Treatment Plant Effluent (PTPE) reports
(c) Daily average obtained from available DMR’s representing less than a
12 month period
(d) Average daily flow stipulated by permit
(e) Maximum daily flows stipulated by permit
Atlantic Richfield Co. (ARCO)
Crown Zellerbach Corp.
Dungeness Salmon Hatchery
Elwha Salmon Channel
Fibreboard Paper Products Corp.
Heart 0’ the Hills Campground
ITT Rayonier, Inc.
M & R Timber, Inc.
Peninsula Plywood Corp.
Port Angeles Car Wash
Port Angeles STP
Pres—Sure—Matic, Inc.
U.S. Coast Guard Air Station
<.0001(a) closed
9.81 10.66
15.00(d) 15.00(d)
32.00(d) 32.00(d)
N/A N/A
.007 .056
36.67 40.19
.077(e) .077(e)
.090(e) .090(e)
N/D HID
3.15 2.88
.0015(e) .0015(e)
<.0001(d) <.0001(d)
N/A N/A
6.11 6.74(c)
15.00(d) 15.00(d)
32.00(d) 32.00(d)
N/A N/A
.008(e) .008(e)
38.41 41.80(c)
.077(e) .077(e)
.090(e) .090(e)
N/D N/D
1.99 2.50(c)
.0015(e) .0015(e)
<.0001(d) <.0001(d)

-------
Figure lI-S. PORT ANGELES MONTHLY AVERAGE FOR EFFLUENT FLOW.
(a) Refer to text to determine monitored outfalls.
source: Available DMR’a on file at r’ , Lacey, Washington or EPA, Region X, Seattle, Wa.
44
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-------
Available data shows that the two fish hatcheries in the area
were major contributors of flows to the receiving waters from
1975 to mid 1980 (32 mgd (121.1 mid) for Elwha Hatchery and 15.00
mgd (56.78 mid) for Dungeness Hatchery) (Table 11-2). In
contrast, the city of Port Angeles STP (1969 — mid 1980) aver-
aged 2.45 mgd (9.28 mid) (Table 11-2). All other dischargers
are minor by comparison, with average daily flows of less than
0.1 mgd (.38 mid) (Table 11—2).
Suspended solids, spent sulfite liquor (ssL), concentrations of
organic material measured as BOD, zinc, and various inorganic
constituents are discharged by the Port Angeles area pulp and
paper mills. Additionally there are various toxic organic
constituents of unknown concentration discharged by these mills.
Chlorine, bacteria and nutrient discharges enter the Harbor from
municipal and domestic STP’s. The main waste constituents of
the minor industries consist of suspended solids and small
amounts of oil and grease. Prior to the installation by
Peninsula Plywood of a recycle system, glue wastes were also
discharged to the Harbor. Fish wastes such as ammonia nitrogen
and fish food (suspended and settleable solids) are the main
hatchery wastes (CH2M Hill 1974, ENCON 1974).
1. Crown Zellerbach
In accordance with waste discharge permits issued to the mill
between 1956 and 1970, Crown Zellerbach was required to submit
a monthly summary of the daily monitoring (all monthly summaries
submitted by the mill are referred to as discharge monitoring
reports (DMR) unless indicated differently) on specific effluent
characteristics to the Washington Pollution Control Commission
(WPCC), predecessor to DOE. Beginning in 1971 all DMR’s were
required by permit to be submitted to DOE. The averaae and
maximum effluent limitations for specific parameters (BOD, SCS,
TSS, zinc and pH) were first required by the National Pollutant
92

-------
Discharge Elimination System (NPDES Permit No. WA 000292-5
(issued December 31, 1974). Previous permits specified only
a limit for a maximum waste flow. The frequency of sampling
was determined by permit requirements; however beginning in
1975 the permit designated both the frequency and type of
sampling. Crown Zellerbach’s available DMR’s provide infor-
mation on eight effluent characteristics (flow, production,
TS, SCS, TSS, BOD, zinc, and pH). The following text provides
an analysis for those parameters with specified permit limits
in reference to their discharged quantities and requirements
during mill operation.
During the 1966 - mid 1980 period, Crown Zellerbach maintained
an operative effluent flow averaging 8.89 mgd (33.65 mld)
(Table 11—2, Figure 11—5). From 1966 to November 1971 mill
flows and other parameters were monitored and recorded from
the groundwood pulp mill (stone screening) and the old mill,
new mill, No. 1 saveall, No. 2 saveall, and No. 3 saveall of
the paper mill complex. Subsequent to the start-up of primary
treatment facilities (November 1971) available DMR’s provide
information only on the primary treatment plant effluent(014).
Beginning July 1977 the flow for the filter plant backwash
(020) was also provided.
Crown Zellerbach’s primary treatment facilities were operable
as of November 22, 1971 (Kendall, letter of November 24, 1971).
The system removed both settleable and floating solids. Since
all the monitored mill outfalls previous to primary installation
may not have been combined into outfall 014 (the only monitored
outfall in available information after November 1971), an
accurate analysis of possible reductions in SCS and PS attributed
to primary treatment cannot be obtained (Figures 11-6, 11-7).
93

-------
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Figure 11-6. CROWN ZELLERBACH MONTHLY AVERAGE - SCS
Source: Available DMR’s on file at DOE, Lacey, Washington
or EPA, Region X, Seattle, Washington
essv
isse i e ee
- isio
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ten
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—
1975
iii -
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ten
teso
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———Permit Requirements - Daily Average Limit
(lbs/day)

-------
Figure 11-7. CROWN ZELLERBACH MONTHLY AVERAGE - TOTAL SOLIDS
Source: Available DMR’s on file at DOE, Lacey, Washington
or EPA, Region X, Seattle, Washington.
1iat
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-------
Replacement of the zinc hydrosulfite bleaching process with
the Ventron process (July 1977) decreased zinc contained in
discharged effluents to less than the maximum 56 lb/day
(25.4 kg/day) permit requirement (Figure 11-8). From 1972
to 1976 the mill, discharged approximately 739 lbs/day (335
kg/day) based on operative yearly averages (Figure 11—8).
Subsequent to July 1, 1977 the mill was to sample once a
month (24 hour composite) to determine compliance with per-
mit limitations. From August 1977 to May 1980 the highest
maximum zinc discharge occurred in June 1978 and December 1979
(3], lbs/day)(14.06 kg/day).
During the 14 month period (July 1977 - August 1978) follow-
ing non-compliance with secondary treatment installation,
excessive quantities of BOD loadings were discharged to the
Class AA waters of the Strait (Figure 11-9). During this
time period the average BOD discharge (14,893 lbs/day) (6756
kg/day) exceeded the required monthly average of 7,000 lbs/day
(3175 kg/day) by approximately 11,3 percent (Figure 11—9).
Following the start—up of secondary treatment facilities
(September 1978) a significant decrease in effluent BOD dis-
charged from 001 is noticeable (Figure 11—9). A major strike
causing partial shut down of the mill contributed to this re-
duction between September 1,978 to January 1979; however from
February 1979 to May 1980 mill, production was normal and the
BOD remained at a decreased level (Figure 11-9). From 1972 -
1977 the average BOD discharge was 13,109 lbs/day (5,946 kg/day)
based on operative yearly averages as compared to 3,146 lbs/
day (1,427 kg/day) discharged during 1979.
Beginning July 1, 1977 Crown Zellerbach was required to monitor
TSS as opposed to previous requirements for SCS monitoring. As
a result of the high content of clay in pulp produced by the
Crown Zellerbach mill, the TSS values are considerably greater
than previous SCS values (Rock, personal communication of
96

-------
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INS ] 1957 N . _________I *io ]_________
• YEARS
Figure 11-8. CROWN ZELLERBACH MONTHLY AVERAGE - ZINC
Source: Available DMR’s on file at DOE, Lacey,
Washington, or EPA, Region X, Seattle,
Washington.
43-I- 4.Oa 4*II Oa “4O I4 •
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197 9
C—-.- ’ Permit Requirements -
Daily Average Limit (lbs/day));
(a) Maximum Permit Requirement (lbs/
day). therefore 7/77 - 5/80 repre-
sents maximum zinc discharge.

-------
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$ 577
YLAMS
Figure 11-9. CROWN ZELLERBACH MONTHLY AVERAGE - BOD
Source: Available DMR’s on file at DOE, Lacey, Washington
or EPA, Region X, Seattle, Washington.
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-------
April 4, 1979). During the 14 month period prior to
secondary treatment (July 1977 - August 1978) the mill
discharged an average of 9,224 lbs/day (4,184 kg/day) TSS
based on monthly operative averages (Figure 11—10). During
1979 the mill discharged approximately the same daily quan-
tity (8,303 lbs/day) (3,766 kg/day) (Figure 11—10). This
indicates that the bacteria introduced into the effluent in
the aeration tanks (secondary treatment) is sufficiently
removed in the secondary clarifier. From July 1977 to May
1980 the mill exceeded their average TSS limitation of
10,000 lbs/day (4,536 kg/day) on six occasions (Figure 11—10).
Crown Zel].erbach was first required to monitor pH on July 1,
1977. Beginning on this date the mill effluent was required
to maintain a pH of 5 - 9 on a daily basis. Due to the
extensive data base and requirement for daily monitoring as
opposed to monthly averages of daily results the data is not
graphed in this section. An anlysis of the data indicates
the mill violated the pH range on 15 occasions (Appendix I—F,
Tables I—F—B, I—F—9).
2. Fibreboard
Fibreboard’s sulfite mill discharged wastes to the Harbor from
1917 to November 1970. Compared with ITT Rayonier and Crown
Zellerbach, Fibreboard (1966 — 1970) produced the lowest aver-
age daily flow (3.52 mgd) (13.34 mid). During the 1960’s, BOD,
SCS and TS loads were required to be monitored from each out-
fall and submitted monthly to the WPCC. Monitoring reports
prior to 1966 could not be located on file at DOE, Lacey, Wash-
ington or EPA, Region X, Seattle, Washington; therefore all
information is derived from 1966 — 1970 data containing only
flow, pulp production, SCS and TS.
Compared to the other two Port Angeles mills, Fibreboard pro-
duced the lowest SCS (4,382 lbs/day) (1,988 kg/day) discharge
99

-------
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1161
1661
1966
1170
1971
1972
1673
1974
1979
ii.
YEARS
Figure 11-10. CROWN ZELLERBACH MONTHLY AVERAGE - TOTAL
SUSPENDED SOLIDS
Source: Available DMR’s on file at DOE, Lacey, Washington or
EPA, Region X, Seattle, Washington.
I ...
. 4+. L 4
ii tI ft
titi1 ii
iii
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(—— Permit Requirements -
Daily Average Limit (lbs/day)).

-------
from 1966 to 1970 (Figure Il-li). During this same period
Fibreboard was second to ITT Rayonier in the operable yearly
average of TS produced by the mi i i. (95,497 lbs/day) (43,317
kg/day) (Figure Il-il). Effluent BOD values if monitored were
never formally submitted to WPCC. Fibreboard and ITT Rayonier
were the only industries discharging spent sulfite liquor
(SSL) to the Harbor; however no SSL monitoring requirements
were demanded of the mill during its history. As a result, no
conclusive comparisons can be made regarding this parameter.
Fibreboard was required to install primary treatment by Sept-
ember 30, 1970. The mill did not proceed with construction
and closed in November 1970.
3. ITT Rayonier
Previous to September 1, 1974, ITT Rayonier was required by
state waste discharge permits to submit a monthly summary of
the daily monitoring (all monthly summaries submitted by the
mill are referred to as DMR’s unless indicated differently)
on specific effluent characteristics to the WPCC. Upon issuance
of ITT Rayonier’s first NPDES Permit No. WA 000079_8, issued
August 30, 1974, the mill was required to submit DMR’s to DOE.
Both average and maximum effluent limitations for specific
effluent characteristics (SOD, SCS, TSS, SSL and pH) were first
required in this permit; however previous permits did designate
a maximum limit on waste flow. Unlike previous state permits
which designated frequency of sampling effluent characteristics,
the NPDES permit specified both frequency and type of sampling
to be conducted for each parameter. The available DMR’s sub-
mitted to the appropriate agencies provide information on nine
effluent parameters (flow, production, TS, SCS, TSS, BOD, SSL,
pH and temperature). The mill 1 s permit standards and effluent
quantity and/or quality for those parameters with specified
permit limits are analyzed in the following text.
101

-------
Figure 11-li. FIBREBOARD MONTHLY AVERAGE - SCS
Source: Available DMR’s on file at DOE, Lacey, Washington
or EPA, Region X, Seattle, Washington.
oo
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000C
oc
68
640C
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1570
1571
1973
1 173
1974
1975
1915
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IllS
19Th
1110
TIARS
I
i1
flu

-------
Figure 11-12. FIBREBOARD MONTHLY AVERAGE - TOTAL SOLIDS
Source: Available DMR’s on file at DOE, Lacey, Washington
or EPA, Region X, Seattle, Washington.
2 O
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TH1MTr
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-------
ITT Rayonier, the major discharger of industrial waste
waters into the Harbor, maintained an average flow of 35.87
mgd (136.8 Mid) from 1966 to June 1980 (Table 11-2, Figure
11—5). From 1966 - September 6, 1972, when the submerged
outfall became operative (DMR September 1972) flows and other
characteristics were monitored from outfalls: A(00l) Log
Barkers, B(002) Screen Room, C(003) Blowpits and part of the
Bleach Plant effluent, D(004) remainder of Bleach Plant ef flu-
ent and E(005) miscellaneous effluent. In addition to these
five outfalls, mill flows monitored from October 1970 to
September 1972 also included the Filter Plant Backwash Plant.
Subsequent to September 1972 until January 1973 effluent para-
meters were recorded from four outfalls: C(003A) Blowpits, E(005)
miscellaneous effluent, BW(006) Filter Plant Backwash, and the
submerged outfall (S.C. 007). The outfall E(005) components
were rerouted to different outfal].s by January 22, 1973 (DMR
January 1973); therefore monitoring was conducted on 003A,
006 and 007 until January 1, 1975 when 006 was no longer in use
(DMR January 1975). Beginning September 1975 to June 1980
monitoring was provided for only one operating outfall dis-
charging residual mill wastes, 007 (now 001).
Between 1966 and October 1971 (Crown Zellerbach installed
primary treatment facilities November 1971) the average SCS
load discharged by ITT Rayonier (44,160 lbs/day) (20,031 kg/day)
was approximately 64 percent greater than that of Crown Zeller-
bach (26,987 lbs/day) (12,241 kg/day) based on operative
yearly averages (Figures 11—13 and 11-6). Available information
does not indicate the percent of Crown Zellerbach’s effluent
diverted to the Harbor or Strait, but information implies that
most of the mill’s fiber bearing wastes were discharged to the
Strait during this period (Refer to Section I.A.1, Tables 1—2,
1-3, and Figure 1-2). From 1966 to 1970 ITT Rayonier’S SCS
discharges (45,616 lbs/day) (20,692 kg/day) based on operative
yearly averages exceeded by more than ten times the amount dis-
charged by Fibreboard (4,382 lbs/day) (1,988 kg/day) (Figures
11—13 and II—i1 -
104

-------
1999 1
INI
N f
197 f 1971 1972
1973 174 1975
11179 j 1977
1Th
-
YEA $ (——--Permit Requirements —
(a) Stipulation No. 9586 required operable compliance 12/31/74 but NPDES Permit No. WA 000079-5
required operation 4/1/75.
(b) Initial start-up.
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Figure 11-13. ITT RAYONIER MONTHLY AVERAGE - SCS
4. 4.oac
Daily Average Limit (lbs/day));

-------
A comparison of TS values shows ITT Rayonier contributed the
greatest quantities to the study area. From 1966 to 1970
Fibreboard discharged to the Harbor an average of 95,497 lbs/
day (43,317 kg/day) compared with 1,625,108 lbs/day (737,149
kg/day) contributed by ITT Rayonier (Figures 11-12 and 11—14).
During this same period Crown Zellerbach discharged approxi-
mately 58,960 lbs/day (26,740 kg/day); however information is
not available on the amount of this total that was discharged
to the inner Harbor (Figures 11-7 and 11—14).
In September 1972 primary treatment facilities and submerged
outfall 007 began operating. Despite the fact the mill divert-
ed additional waste flows to 007 which had not been monitored
previously (see Section I.C.1) and in October 1972 effluent
characteristics from 006 began to be recorded, the SCS and TS
levels discharged by the mill still showed a reduction subse-
quent to primary treatment operation (Figures 11-13 and 11-14).
The mill’s SCS discharge was reduced from an operative yearly
average of 44,182 lbs/day (20,041 kg/day) (1966 — 1971) to
8,533 lbs/day (3,871 kg/day) (1973 — 1978) . The limited TS
data was not significantly reduced following start-up of primary
treatment facilities (Figure 11—14).
Following Fibreboard’s closure in November 1970, ITT Rayonier
was the single contributor of significant waste loads of SSL
into the Harbor until September 1975. At this time all of the
mill’s residual wastes were diverted via a submerged outfall to
the Strait, east of Port Angeles Harbor. ITT Rayonier initiated
operation of their Chemical Recovery System on January 16, 1975
(Stolz, letter of February 10, 1975). This system was to reduce
the mill’s discharge of SSL and BOD; however, available informa-
tion indicates that problems continued to plague the system
(Section IC.1 and C.3). Prior to December 1975 the mill was not
required by permit to report SSL quantities discharged by the
mill. Subsequent to this date the mill was to monitor daily
106

-------
Source: Available DMR’s on file at DOE, Lacey, Washington
or EPA, Region X, Seattle. Washinaton.
31
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Figure 11-14. ITT RAYONIER MONTHLY AVERAGE - TOTAL SOLIDS
1
I -
N
1971
1912
1973
1974
19Th
1979
IS??
f 1519
[ 1979
I
11
. I41 ,,4mOSl
YEARS
Iii
(* = Estimate)
I
• 1 . .I41- • ,4s lQ
I S j

-------
discharges of SSL solids and not exceed a 14—day moving
average limit of 247,000 lbs/day (112,000 kg/day). Stipulation
No. 9586 which was incorporated into Permit No. WA 000079-8,
Condition 2 also required the mill to limit its SSL solids
discharge to 15% or less of the total SSL solids generated
and not exceed 312,000 lbs/day (141,523 kg/day). During
tne periods of time in which the two different maximum
limits were in effect (December 1975 - July 1977), the
more stringent limit was to be followed to determine violations
(Permit No. WA 000079— , modified 10/22/75). Due to the
availability of SSL solids data 14-day SSL moving averages
were reviewed from June 1977 to July 1979. Violations of
the SSL requirements during this period are summarized in
Table 1—12, and Appendix I-M, Table I-M-2.
Despite the problems with the Chemical Recovery System, BOD
was gradually reduced to an average of 220,541 lbs/day
(100,030kg/day) to the Strait (Figure 11-15). During this
same period (1976 — 1978) Crown Zellerbach discharged 12,597
lbs/day (5,714 kg/day) of BOD to the Strait (Figure 11-9).
In order for ITT Rayonier to comply with BOD and pH permit
limits, the mill was required to install and operate secondary
treatment facilities or its equivalent by July 1, 1977. Oper-
ational compliance was not achieved until October 12, 1979.
During this 27 month period the mill violated its average and
maximum BOD and minimum pH limits almost constantly (Tables
1-12, I-M-3, I-M-4, I-M-l0). A comparison of average BOD
loads before treatment (174,440 lbs/day) (79,125 kg/day)
(January — September 1979) and after treatment installation
(46,978 lbs/day) (21,309 kg/day) (October 1979 - June 1980) shows
a reduction of approximately 75 percent (Figure 11-15). Due
to its extensive data base (reported daily) pH is not graphed
in this section; however subsequent to secondary treatment
operational compliance with the pH standards improved
103

-------
‘1
II •1 I
YLAR$
Figure 11-15. ITT RAYONIER MONTHLY AVERAGE - BOD
(a) Stipulation 9586 required operable compliance 12/31/74,
(b) Initial start—up,
(c) EPA required mill to abide with the expired Permit (No. WA 000079-5)
limits until a new permit was in effect.
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( -—Permit Requirements -
Daily Average Limit
I
(lbs/day));

-------
significantly (Tables I-M—9, I—M—10). Since October 12,
1979, the pH range has been violated by the mill on thir—
teen occasions (Tables I—M—9, I—M—l0).
The mill was required to monitor TSS in place of SCS as of
July 1, 1977. ITT Rayonier did not initiate this monitoring
until October 1979. The lack of an extensive TSS data base
does not allow for an analysis of this information in refer-
ence to secondary treatment operation (Figure 11-10).
4. Other Industrial and Municipal Dischargers
In addition to the Crown Zellerbach and ITT Rayonier pulp and
paper mills, a minimum of 8 facilities discharge industrial,
municipal or domestic waste waters to the Harbor or Strait.
In addition to these direct discharge points, a minimum of 24
additional industrial ground dischargers exist in the area
(Pres—Sure—Matic, Inc. ,wood waste fills, log yards, and a land-
fill). The following portion of this section is divided into
categories representative of specific facilities known to dis-
charge to the study area as of 1975 (Table 11—1, Figure 11—2).
These include the following categories: wood processing, fish
processing, vehicle washing, miscellaneous and domestic or
municipal facilities. The ground dischargers in the area do not
discnarge directly to a receiving water, but do require consid-
eration as potential contributors to water quality degradation
in the adjacent receiving waters of the Strait or Harbor.
Those ground dischargers active as of 1980 are discussed in a
separate category (ground dischargers) and located on Figures
11—2, 11—3, 11—4). In addition to ground ciiscliarges, log
rafting and storage in waters of the Harbor are discussed
as non-point source dischargers.
Wood Proceseing: There are two wood related industries
(Peninsula Plywood and M & R Timber) presently discharging
110

-------
(a) EPA required mill to abide with the expired Permit
(No. WA-000079-5) limits until a new permit was in effect.
Daily Average Limit (lbs/day));
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Figure 11-16. ITT RAYONIER MONTHLY AVERAGE TSS
I .•I
II
1*54
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IllS
1*70
1*71
1173
1*73
1*74
1*7 5
t 75
1 *77
1*7 5
* 57 *
k
YEARS
1
-I a4* -I4 os
L—’----Permit Requirement
1 5 4 0

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non-contact cooling waters to the Harbor. Available infor-
mation indicates Peninsula Plywood Corporation began operation
in 1941 (Application No. WA 003805-9, December 20, 1974)
and on October 25, 1975 this plywood manufacturing company be-
came a division of ITT Rayonier (Berner, letter of January 21,
1976)
The major wastes contributed to receiving waters by this facil-
ity included glue solids, boiler blow-down waters and surface
oil (Permit No. WA 003805—9,July 9, 1975). By the mid 1970’s
and possibly sooner Peninsula Plywood diverted some of their
process wastes to the Port Angeles STP. The remainder of the
discharge was sent to the mill, pond for settling prior to dis-
charge (outfall 002) (Application No. WA 003805-9, Decem-
ber 20, 1974). By January 1977 the glue wash water wastes were
being recycled, eliminating the discharge of glue wastes to
the Harbor (Helle, letter of December 28, 1977). Most of the
boiler blow—down wastewater discharge was eliminated by May
1977 (Springer, Inspection Report of May 23, 1977). Due to the
elimination of these discharges, non—contact cooling water is the
major effluent constituent discharged from 001 and the mill
pond area, 002. Available DMR’s (1977 — 1979) show this dis-
charge to be free of oil and grease, parameters required by
permit to be monitored. There is a small amount of untreated
back flush wastewater discharge to 002; however analysis indi-
cates the discharge contributes no toxic substances to the re-
ceiving waters and therefore is not included in the mills cur-
rent NPDES permit (No. WA 303805—9)(Uelle, letter of June 30, 1977).
The majority of logs received by Peninsula Plywood are trucked
from their storage site where the logs are stored and sorted
(Figure 11—4). Due to space limitations the logs are tempor-
arily stored on the Peninsula Plywood tail], site grounds before
being processed into plywood. As of late 1977, run—off from
112

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the mill site log yard was diverted to the corporation’s
controlled mill pond area (002) before entering open water
(Heele, letter of December 28, 1976).
M & R Timber, Inc. uses logs to manufacture softwood lumber
and chips (DOE 1974). Since September 1974 and possibly
earlier, M & R Timber has utilized 3 outfall sources to dis-
charge non-contact cooling or compressor water to the Harbor
(001, 003, 004) (Application No. WA 003784—2, September 2,
1974). A fourth source discharges run-off from precipitation
(002). In addition to the cooling water, outfall 001 also
discharges a small amount of water used to dampen logs and
cool the chip, saw and edger blades (Application No. WA
003784—2). According to an analysis of the untreated effluent
from 001, the discharge is low in pollutants and requires no
treatment (Stroble, letter of March 24, 1976; Owens, letter of
September 16, 1975). Application No. WA 003784-2 indicates
these four point sources were active in 1958 but the available
information does not indicate the quality of the discharged
effluent until September 2, 1974, the Application Date.
The majority of logs are trucked to M & R Timber from their
log storage yard for temporary storage before being processed
(Figure 11-4). According to permit requirements (No. WA
003784—2) the mill was to submit a plan and schedule by August 1,
1976 to DOE to meet the following limitations for their mill
site log yard:
• Turbidity - A dilution Zone of radius 150 feet
surrounding outfall 002 is allowed.
Shall not exceed 5 JTU over natural conditions outside
this dilution zone.
• Settleable Solids - Shall not exceed 0.1 mg/i
• Floating Material - A method/device shall be employed
to prevent the discharge of floating matter.
• Oil - Shall not average more than 10 mg/i with no
single sample exceeding 15 mg/i. No visible sheen
shall be present at any time.
113

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Fi .ah Rearing: Two fish rearing facilities are operating on
tributaries located on the east (Elwha Salmon Channel) and
west (Dungeness Hatchery) borders of the study area. The
Elwha Rearing Channel began operation in mid 1975 (DOE (a)
no date). Available information describes a start-up date
for the Dungeness Hatchery as 1902 with reconstruction occur-
ring in 1947 (Application No. WA 003833-4). The Elwha Salmon
Channel consists of one elongated channel for rearing chinook
and coho while the Dungeness Hatchery has raceways and a rearing—
release pond for chinook and coho salmon (DOE (a) no date;
DOE (b) no date).
The rearing pond and channel in these hatcheries consist of a
one-time flow—through system diverting water from the respec-
tive river through the rearing area and returning the untreated
water back to the receiving waters (Wood, personal communication
of October 10, 1980). A small amount of the fish food waste
products are contained in this discharged effluent, but analy-
sis has shown that the fish and food waste products dissipate
quickly and do not cause a water quality problem to the Dung-
eness and Elwha Rivers (Wood, personal communication of October
10, 1980). When the juvenile salmon are ready for release, the
rearing channel or pond is drained and the fish released in a
controlled manner so as not to exceed 3.3 ml/liter of settleable
solids at any time (Permit No. WA 003833-4 and Permit No. WA
003803—2). Once the channel is drained the remaining solids
are removed and discharged on land (Uood, personal coimnunica-
tion of October 10, 1980).
The sixteen raceways located in the Durigeness Hatchery also
have a one—time flow—through system. In order to comply with
the daily maximum permit limits for SS (3200 lbs/day) (1,451
kg/day) (15 mg/i) and settleable solids (0.2 mi/i to be obtained
during cleaning), each raceway is brushed down once a week,
one at a time, and the solids are washed into the Dungeness
River (Wood, personal communication of October 10, 1980).
114

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Vehicle Washing: In the Port Angeles area only one vehicle
washing facility is required to operate in accordance with
an NPDES permit (Pres-Sure-Matic, Inc.). This log truck
washing facility caused turbidity and oil problems to Turn—
water Creek until late 1974 when a series of 3 settling basins
were installed (DOE (c) no date; Application No. WA 003772-9).
In addition to the settling basins, baffles were included to
skim oil from the surface of waste water before the effluent
was discharged to Tumwater Creek (Olsen, letter of August 22,
1974). Available correspondence indicates the facility instal-
led a recycle system; however by 1977 the system ceased to
function properly (Springer, letter of July 26, 1977; Olsen,
letter of August 22, 1974). Proper operable recycling facil-
ities to allow discharge to the ground were not installed until
sometime after 1978 (Greiling, letter of August 8, 1978). As
a result this facility frequently discharged muddy effluent to
Tumwater Creek during this two year period (1977 — 1978) and
possibly longer (Greiling, letter of August 8, 1978).
A vehicle rinsing facility (Port Angeles Car Wash) located
at the base of Ediz Hook was operating in the study area
prior to its 1977 closure (Monahan and Pierce, personal com-
munication of August ii, 1980). This facility provided
automatic rinsing to remove salt and sand from cars driven
on Ediz Hook (DOE (d) no date). The rinse water was dis-
charged into Crown Zellerbach’s log pond. According to
a DOE evaluation (d) (no date), the facility had no signif-
icant impact on water quality.
Miscellaneous Industries: During ARCO’s operation (June 1952 —
November 1976) the facility stored petroleum products in tanks
before redistribution in bulk to consumers (Application No.
071—OYB-2-000].35). Storm water impounded by firewa].ls sur-
rounding the storage tanks was diverted to a settling sump
before being discharged to the Harbor (Application No. 071-
OYB—000135). In accordance with NPDES Permit No. WA 000142—2
issued July 23, 1975, monthly grab samples of the effluent were
not to contain more than 15 mg/i.
115

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The U.S. Coast Guard Air Station located on the east end of
Ediz Hook discharges treated oily wastes from bilge tanks (Out-
fall 001) and runway run-off water (outfall 002) to the Harbor
(Permit No. WA 002427—9). The bilge tank effluent is diverted
to a mechanical oil separator previous to discharge, whereas
run-off water receives treatment in an Apron Gravity Separator
before flowing to the Harbor (Permit No. WA 002427—9). Oil and
grease limitations on effluent from 002 require a daily average
of 10 mg/l (Permit No. WA 002427-9) . NO limitations for these
parameters were stipulated for outfall 001.
Dungeness Oyster Farm located near the mouth of the Dungeness
River discharges wash waters generated during the shucking and
packing of oysters (ENCON 1974). An NPD.ES permit was issued to
the facility in July 1974; however no treatment of the discharge
was required (ENCON 1974). The oyster farm discharges approxi-
mate].y 250 gallons per day (ENCON 1974).
Municipal and Domestic Facilities: In this report municipal
and domestic facilities are differentiated according to the
waste received by each. Municipal refers to a STP receiving
and treating sanitary and industrial wastes. Domestic facili-
ties only receive and treat sanitary wastes.
The Port Angeles STP began operation in 1969 (DOE Ce) no date).
Prior to this date all domestic sewage was diverted to the Har-
bor (DOE (e) no date). Presently the Port Angeles STP subjects
incoming effluent to primary treatment (sedimentation and chlori-
nation) before discharging to an extended submerged outfall (001)
located at the Harbor’s entrance (Robinson, personal communica-
tion of October 14, 1980; Application No. WA 002397—3). In addi-
tion to the submerged outfall (001), seven additional overflow
lines are utilized when necessary by the Port Angeles STP (Appli-
cation No. WA 002397-3). The settled primary sludge is digested
and disposed on land (DOE 1977). Secondary facilities will be
constructed by the plant when P.L. 92—500 federal grant money be-
comes available (Robinson, personal communication of October 14,
1980)
116

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This STP primarily receives domestic sewage with some mixture
of storm water (DOE Ce) no date). Only minimal amounts of in-
dustrial wastes are diverted to the plant for treatment (DOE
Ce) no date).
The current NPDES permit (No. WA 002397-3) requires the plant
to maintain a monthly BOD and SS average of 1,211 lbs/day
(549 kg/day) or 15% of the respective influent concentrations
using the more stringent requirement during dry weather months.
The monthly average limit for fecal coliform bacteria is 200-
100 ml. Chlorine residual is required to be sampled continuous-
ly but there is no designated limitation in the permit.
Heart 0’ the Hills campground is located approximately 5 miles
south of Port Angeles in the Olympic National Park. The camp-
ground consists of 100 campsites and 5 comfort stations (EPA,
no date). Major waste flows from the campground occur in the
summer months with limited discharge in the spring and fall
(Olympic National Park Service personnel, personal communica-
tion of 1979)
During the early operations of the campground, sanitary wastes
from the comfort station were treated in an extended aeration
system and chlorinated before discharging to Ennis Creek (Olym-
pic National Service personnel, personal communication of 1979)
Soon after 1974 the system was upgraded with a sand filter unit,
surge tank, sludge storage tank and emergency chlorination cham-
ber (EPA, no date; Olympic National Park Service personnel,
personal communication of 1979). -
According to ENCON (1974) this upgraded system was comparable
to tertiary treatment. The treated effluent sludge is trucked
to a landfill (ENCON 1974). According to the most recent per-
mit ( No. WA 002446—5) BOD and SS are not to exceed a monthly
average of 0.66 lbs/day (.30 kg/day) and not exceed 5% of the
raw influent of BOD and SS. Chlorine residual is to be moni-
tored daily using a grab sample but no limits are designated
in the permit.
117

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Ground Dischargers: Excluding Pres—Sure—Matic, Inc., there
are a minimum of 23 ground dischargers in the study area (Figure
11-4). The majority of these (22) are represented by log yards
or wood waste fills. The wood waste fills contain scrap wood
from construction sites, dry wall scraps and other miscellaneous
wood wastes (Wood, personal communication of August 11, 1980).
The DOE has conducted specific monitoring on the run—off from
these fills and found them to generally be slightly acidic,
high in color (dark brown to black) and to have a Pearl Benson
Index (PBI) (based on 10% solids base) ranging from 30 mg/i to
as high as 90,000 mg/i in one case (Wood, personal communica-
tion of August 11, 1980). The PBI results indicate the presence
of lignin sulfonates, other lignins, tannins, cresols, natural
plant extracts, phenol and aromatic and aiphatic amines (Feli-
cetta et al. 1963; Clemetson 1967). Surface run—off from the log
yards and Port Angeles landfill also contribute components to
the ground. Then lateral surface dispersion of run—off from
any of these areas does not seep through the ground then nearby
tributaries are susceptible to receiving the untreated run—off.
Additional information on these ground dischargers is on file
with the Solid Waste Permits Division, Southwest Region, DOE,
Olympia, Washington.
Non-point Sources: The Harbor is considered one of the three
principal log rafting areas in the North Olympic Coastal Basin
(ENCON 1974). The majority of these logs are for export; how-
ever ITT Rayonier also receives some logs by way of water
(Fenske, personal communication of October 14, 1980). M & R
Timber and Peninsula Plywood receive logs by water infrequently,
if in fact at all (Wood, personal communication of October 14,
1980).
Based on the review of a recent report, ENCON (1974) reported
the following conclusions on water storage and rafting of
Douglas Fir logs:
118

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1. Water storage of logs is widely practiced in
Oregon, Washington and Alaska.
2. Leachates from logs held in water storage con-
tribute organic substances which exert a BOD
and COD. In most situations the quantity of
these substances which enter the holding water
do not represent a significant water quality
problem.
3. Log leachates exert some acute toxicity to fish.
4. Color-producing substances measured by the PBI
are found in log leachates and are derived pri-
marily from bark.
5. Bark is dislodged from logs in significant quan-
tities during dumpings and raft transport activi-
ties. Considerably more bark is dislodged from
Douglas fir logs than from ponderosa pine logs.
6. Log dumping methods significantly influence the
amount of bark which is dislodged from logs.
7. Dislodged bark sinks at a rate dependent upon
particle size and species of tree.
8. Bark deposits exert a small, but measurable,
demand for oxygen from overlying waters.
9. Should the loss of bark to holding water be mini-
mized by improved handling practices by the timber
industry, the water storage of logs would not con-
stitute a major water quality problem.
Approximately 10 percent of the bark loosened from the logs
sinks within the first day after dislodgement (ENCON 1974).
Any bark that is not displaced by tidal, current or wave
action will, eventually sink to the bottom (ENCON 1974). As
a result periodic dredging of log rafting areas should occur
to avoid interference with marine organisms.
When the logs are in the water, wood sugars and other sub-
stances leach from the wood entering the surrounding water
(ENCON 1974). Based on this information, it was concluded
that chemical oxygen demand (COD), PBI, total volatile solids
(TVS), and total organic carbon (TOC) entered receiving water
from tfle log-rafting of Douglas fir (Table 11-3).
119

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Table 11-3. ESTIMATED POLLUTANTS TO PORT ANGELES HARBOR FROM LOG RAFTING
(Douglas Fir Logs - 2 Ft. Diam. - 30 Ft. Long)
Source; ENCQN 1974
Segment
Water
Exposure
Periods
(days)
COD
M—1
bs.
PBI
M—l
be.
M-l
bs.
M—l
bs.
100%
Bark
50%
Bark
100%
Bark
50%
Bark
100%
Bark
50%
Bark
100%
Bark
50%
Bark
Port Angeles
Harbor
10
153
173
282
184
174
185
51
—
Port Angeles
harbor
35
352
353
726
555
296
265
75
—

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B. MILL CLOSURES
Mill Closure data are important in relation to certain water
quality and bioassay data. The majority of mill closure dates
for ITT Rayonier, Crown Zellerbach, and Fibreboard were obtained
from DNR’s and other effluent data. Written and personal
correspondence were used when available to verify these clo-
sures. Of the three mills, Fibreboard was most frequently
shut—down; final operations ceased on November 25, 1970 (Fibre—
board DMR, November 1970). From 1966 to the present, optimum
production for the ITT Rayonier mill was discontinued during
three separate strikes. Information indicates Crown Zellerbach
was affected by only one strike which occurred from September
1978 to January 1979. Table 11-4 summarizes reported dates
when the various mills were shutdown due to holiday periods,
strikes or other reasons.
The early available effluent data (DMR) for Crown Zel].erbach,
Fibreboard and ITT Rayonier usually provides a daily average
per month for each operable day; however subsequent to 1975
DMR’s only provide the daily averages of monitored parameters
for the entire month. The early DMR’s designate routine clo-
sures for July 4th, Labor Day and Christmas (Table 11—4 ).
During these closures there is no production of mill products
or residual waste flow as reflected in the DMR’s. It is pre-
sumed these routine closures for Crown Zellerbach and ITT Ray—
onier have continued to the present, but there is no available
information in the DMR’s to verify these temporary shutdowns
(1975 — present)
The daily effluent averages per month (DMR) required to be moni-
tored for each mill’s effluent parameters are obtained from the
total operative days during a calendar month (Figures 11-5, 11-6).
Closures and strikes do not decrease daily averages unless the
121

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Table 11-4. SUMMARY OF DOCUMENTED MILL CLOSURES AT PORT ANGELES 1966 - 1979
Mill Routine Closures Closures Strikes
Crown Zellerbach July 4 1966-present Feb. 4,5,11,12 1966 Sept. 1970—Jan. 1979
Labor Day April 10,12 1969 (Rock April 4, 1979)
Christmas April 23—31 1971
Fibreboard July 4 1966-1970 Dec. 2-4, 16-18 1966 None reported
Labor Day March 12-19
Christmas May 16—20
July 2—4, 26—30
Aug. 6
Jan. 14—23 1968
Feb. 20—26
March 9-10, 31
April 1—14
May 26,27, 19—21
Nov. 28—30
Jan. 13—29 1969
Sept. 1—8
Jan. 2—6 1970
April 11—12, 25—27
May 30,31
Aug. 1,2,30
Nov. 25 1970
Indefinitely Closed
ITT Rayonier July 4 1966-present March 26-April 21, 1973
Labor Day April 9-June 17, 1975
Christmas June 23,24, 1976
July 1978-Jan. 1979
(Rock April 4b 1979

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mill maintains a reduced production and is not totally dis-
continued. During Crown Zellerbach’s four month strike
(September 1978 - January 1979) pulp production averaged
approximately 50 percent of the normal operative monthly
value. Reductions in BOD and TSS also occurred during this
period (Figures 11—9, 11—10, Table 11—4). Fibreboard’s
sharp SCS and TS depressions usually correspond with extend-
ed mill closures (Figures lI—il, 11—12, Table 11—4). Pulp
production ceased during ITT Rayonier’s 1973 strike; there-
fore the operative monthly average (March, April) for SCS and
BOD did not decline but the mill did not contribute these
parameters to the receiving waters during the strike (Figures
11—13, 11—15). During the mill’s 1975 strike production
ceased. In 1978, ITT Rayonier’s operative monthly pulp pro-
duction decreased approximately 40 percent during July 1978
to January 1979 which produced an initial decrease in SCS and
BOD (July - August 1978) when pulp production was lowest
(Figures 11—13, 11—15, Table 11—4)
C. EFFLUENT COMPOSITION AND TOXICITY
Available data indicates there are seven known monitored pollu-
tants discharged to the Harbor. These include BOD, SCS, SS,
SSL, chlorine, bacteria and oil and grease. Previous to 1971,
Crown Zellerbach also discharged large quantities of zinc to the
inner Harbor area. Additionally, various classifications of
known toxicants are contained in pulp and paper effluents. These
toxic substances can be divided into organic and inorganic com-
pounds:
Organic Compounds Inorganic Compounds
• Fatty acids (FA) • Heavy metals
• Polar acids (PA) S Metals
• Resin acids (RA) • Chemical additives
• Phenols (P)
• Terpenes CT)
• Juvabiones (J)
• Miscellaneous organic
compounds
123

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Within these two categories the literature permits some divi-
sion into major and minor toxicants. Many compounds, however,
have not been measured as to specific concentration and effects.
The most importantwell known (or suspected) toxicants of sulfite
and mechanical pulp and paper mill effluents are shown in Table
11—5.
Table 11-6 describes the concentrations of 32 organic and 34 in-
organic toxic substances which are found in Crown Zellerbach and
ITT Rayonier effluents. Crown Zellerbach’s organics testing is
limited to monitoring total phenols, while ITT Rayonier ran a
limited series of tests on their organic effluents. Both mills
have performed some testing of metals and other inorganics.
Crown Zel].erbach conducted more tests for inorganic substaz ces
than did ITT Rayonier; however, experimental procedures were
less adequate. ITT Rayonier’s inorganic tests for secondary
treatment were only estimated concentrations until June 1979.
Table 11—7 illustrates various concentrations of other Pacific
Northwest sulfite and mechanical pulp and paper mill effluent
chemicals. Easty, et al. (1978) provided information regard-
ing toxic concentrations after different modes of effluent
treatment. Leach and Thakore. (1977) reported high resin acid
concentrations in mechanical mill effluents. Resin acid values
in primary effluent of sulfite mills are also higher than Easty,
et al. (1978). Thus, it should be considered that effluent
constituents vary from mill to mill, depending on the process
used, wood source, etc.
ITT Rayonier had high concentrations of linolenic, linoleic,
oleic, trichloroguaiacol, tetrachloroguaiacol, and isopiinaric
acids. Their value for dehydroabietic acid was almost 2.2 times
greater than reported by Easty, et al. (1978). Rayonier esti-
mations that concentrations of oleic acid would increase after
124

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Table 11-5. KNOWN AND SUSPECTED TOXIC COMPOUNDS IN MILL EFFLUENT
FOR SULFITE AND THERMOMECHANICAL PULP MILLS
I. MAJOR TOXICANTS :
(Leach and Thakore 1975; Leach et a].. 1976;
and Leach and Thakore 1977)
SULFITE MILLS
Abietic acid (RA)
Dehydroabietic acid (RA)
Isopimaric acid (HA)
Neoabietic acid (HA)
Palustric acid (HA)
Piznaric acid (HA)
Sandaracopimaric acid
II. INTERMEDIATE TOXICANTS : (Leach
et al.
SULFITE MILLS
Juvabione (J)
Juvabiol
Eugenol (P)*
Dehydrojuvabione (J)
Dehydrojuvabiol
MECHANICAL MILLS
Oleic acid (FA)*
Abietic acid (HA)
Dehyroabietic acid (RA)
Isopixnaric acid (RA)
Neoabietic acid (RA)*
Palustric acid (RA)
Pimaric acid (HA)
Levopimaric acid (HA)
Sandaracopimaric acid (RA)*
Pimarol (T)*
Isopimarol (T)*
Ab i eto 1
Dehydroabietol
Palinitoleic (FA)*
Linoleic (FA)*
Linolenic (FA)*
and Thakore 1975; Mueller
1977; Walden and Howard 1976)
MECHANICAL MILLS
Abienol (HA)
Abietal (T)
Juvabione (J)*
12 E - abienol
13 - epiinanool
SULFITE MILLS
Linoleic acid (FA)
Liriolenic acid (FP.)
Palmitoleic acid (FA)
4-4’ dimethoxstilbene (P)
Oleic acid (FA)
I soeugenol
3-3’ dimethoxy - 4-4’
dihydroxys ti ibene
MECHANICAL MILLS
- dehydrojuvabiol (J)
- dehydrojuvabione (J)
Juvabiol (J)
III. MINOR TOXICANTS:
(Leach and Thakore 1975; Leach and Thakore
1977 and Mueller et a].. 1977)
*Toxjcants that were classified in more than one of toxicant
groups I-Ill were entered in this table in the most toxic
group for which it was cited.
125

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Table 11-5. Continued
IV. COMPOUNDS OF UNKNOWN TOXICITY : (Hemingway and Greeves, 1973;
Leach and Thakore 1975; and
Tollefson 1977)
SULFITE MILLS MECHANICAL MILLS
Acetaldehyde (PA) - dehydrojuvabiol
Formic acid (PA) Pimaral
Acetic acid (PA) Isopimaral
Glycolic acid (PA) Methyl dehydroabietate
Methyl glyoxal (RA) Manool
Methyl palustrate (RA)
Methanol (RA)
p - Cytnene CT)
Ace tone
Furfuro 1
5 - methyl furfurol
Furfurol alcohol
Mannose
Xy lose
Arabinose
Vanillan
Vanillic acid
Conidendrin
Todomaturic acid
Mannonic acid
Gluconic acid
Arabonic acid
126

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Table 11-6. CONCENTRATIONS OF PULP AND PAPER MILL EFFLUENT
CHEMICAL
FATTY ACIDS
1) Linolenic Acid
2) Linoleic Acid
3) Oleic Acid
Eugenol.
Trich loroguaiaCOl
TetrachloroguaiacOl
Guaiacol
Phenol
POLAR ACIDS
1) Acetic Acid
2) Formic Acid
3) Acetaldehyde
RESIN ACIDS
1) Dehydroabietic Acid
0.2
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Amberg (1977)
Tollef son (1977)
Folsom & Denison (1976
Tollef son (1977)
Folsor & Denison (1976
Tollefson (1977)
0.1 Tollefson (1977)
Lange 5c Range
CHEMICAL CONCENTRATIONS (mg/L)
CROWN ZELLERBACH (MECHANICAL)
ITT-RAYONIER_(SULFITE)
Influent
10 Effluent
2° Effluenl
l 0 lnfluent
10 Effluent
20 Effluent
x
Range
x
Range
x
0
x
Range
x
PHENOLS
1)
2)
I a
t,J3)
-J
4)
5)
D FPD PJ(’
Tolle fson
To l lefson
Tollefson
(1977)
(1977)
(1977)
73.5
0.2
0.6
0.1
“ ‘5
0.2
0.2
“‘5
100
100
Tr.
0.1
0.3
0.5
“2
0.1
0.1
“2
50
150
0
75, 252
71,264
2) Isopimaric Acid
30
O.1C Tollefson (1977)

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Table 11—6. Continued, page 2
CHEMICAL
RESIN ACIDS (Cont.)
3) Methanol
TERPENES
1) p-Cymene
5-Methyl Furfurol
Mannose
Glucose
Galactose
Xylose
Arab inose
Vanillin
Vanillic Acid
Conidendrin
TodomaturiC Acid
Furfural alcohol
Tr.
15
4
“ .5
340
100
75
70
20
60
150
Tollefson (1977)
Folsom & Denison (1976
Tollefson (1977)
Tollefson (1977)
Folsom & Denison (1976
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
tange
CHEMICAL CONCENTRATIONS (mg/L)
5c Ranqe
CROWN ZELLERBACH (MECHANICAL)
ITT-RAYONIER_(SULFITE)
0 Influent
10 Effluent
2° Effluent
1° Influent
10 Effluent
2° Effluent
ic Ranqe
Range
x
Range
x
Ranqe
x
REFERENCES
35
22, 49
0
OTHER
1) Acetone
2) Furfural
“‘2 Tollefson (1977)
3)
4)
5)
6)
7)
8)
9)
10)
11)
12)
13)
Tr.
10
“2
0
0
0
0
0
30
75
Tr.
Tr.
5
Tr.
Tr.
0

-------
Table 11—6. Continued, page 3
CHEMICAL CONCENTRATIONS (mg/I.)
REFERENCES
OTHER (Cont.)
14) Mannoic Acid
15) Gluconic Acid
16) Xylonic Acid
17) Arabonic Acid
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
Tollefson (1977)
CHEMICAL
anqe
x
Range
x
CROWN ZELLERBACH (MECHflIICAL)
ITT—RAYONIER_(SULFITE)
0 Influent
10 Effluent
2° Effluent
1° Influent
1° Effluent
2° Effluent
Ranae
x
Range x
Ranqe
‘C
Range
‘C
20
20
15
10
Tr.
Tr.
Tr.
Tr.

-------
Table 11-6. Continued, page 4
REFERENCES
Strachila & Hamlin
(1977), Amberg (1977)
Tollef son (1977)
Strachila & Hamlin
(1977)
Strachila & Hamlin
(1977)
Strachila & Hamlin
(1977), Strachila (l97
Strachila & Hainlin
(1977, Strachila (1978.
Strachila & Hamlin
(1977)
Strachila & Hamlin
(1977), inberg (1977)
Strachila & Haznlin
(1977), Amberg (1977)
Tollefson (1977)
Strachila & Hamlin
(1977), I mberg (1977)
Tollefson (1977)
Strachila & Hamlin
(1977)
Young (1975)
Strachila & Hamlin
(1977), Amberg (1977)
Tollefson (1977)
Concen—
CHEMICAL - tration
Range
i Range
CHEMICTtL CONCENTRATIONS
CROWN ZELLERBACH (I4ECHANTCAL)
rrr RAYONIER_(SULFITE)
10 Influent
1° Effluent Effluent
10 Influent
10 Effluent
2° Effluent
R range
x
p
x
Range
x
Range
x
1) Aluminum
2) Antimony
3) Arsenic
4) Barium
5) Beryllium
6) Boron
7) Cadmium
8) Calcium
9) Chromium
Cobalt
Copper
(mg/L)
(mg/L)
(iig/L)
(mg/L)
(pg/L)
(pg/L)
(mg/L)
(pg/L)
(mg/L)
(mg/L)
(pg/L)
(pg/L)
(Iig/L)
(pg/L)
( ig/L)
(pg/L)
2.861
1.0
12.7
10
41
.99—19.1
4—32
4-59
:0.04-0.5
L18—0. 2
:0.4—3.0
.7.0—26.
23—40
3—15
13—25
11.04
0.01
18
:0.01
39.5
<0.35
0.23
<1.7
21.8
12.0
31.5
50
9
19
50
.01
12.0
50
50
50—100

-------
Table 11—6. Continued, page 5
REFERENCES
Strachila & Hamlin
(1977), Auiberg (1977)
Strachila & Hamlin
(1977), Amberg (1977)
Tollefson(1977),
Ainberg (1977)
Strachila & Hamlin
(1977)
Strachila & Hamlin
(1977)
Strachila & Hainlin
(1977), Ainberg (1977)
Tollefson (1977)
Strachila & Hamlin
(1977)
Strachila 6 Hamlin
(1977), Amberg (1977)
Strachila (1978),
Tollefson (1977)
Strachila & Hamlin
(1977)
Tollefson (1977)
Strachila & Hainlin
(1977)
Strachila & Hamlin
(1977), Amberg (1977)
Tollefson (1977)
Concen-
CHEMICAL tration
CHEMICAL CONCENTRATIONS
‘ange
12)
13)
Iron
Lead
Range
x
CROWN ZELLERBACH (MECHANICAL)
ITT-RAYONIER_(SULFITE)
Influent
10 Effluent
2° Effluen
1°Influent
1° Effluent
2° Effluent
Range
x
Range !
Ranqe
14) Magnesium
x
Ranqe
x
15)
-46)
17)
18)
Mangenese
Mercury
Molybdenum
Nickel
(mg/L)
( g/L)
(pg/L)
(mg/L)
(mg/L)
(mg/L)
( g/L)
(ug/L)
(pg/L)
(pg/L)
(pg/L)
(mg/L)
(mg/L)
(pg/L)
(mg/L)
(mg/L)
4. W
1:
2.’
p.54
7
1.36
.34—10.90
10-29
.54—6.09
.49-0.69
:0.1—0.2
16—65
0.56—0.82
19) Nitrate
4.57
24
3.0
4.82
0.59
0. 15
<0.1
<0.3
19. 5
40
<1.0
0.2
5.0
0.69
0.01
20)
21)
Nitrite
Phosphorus
2.0
<0.1
40
.0
“4.0

-------
Table 11-6. Continued, page 6
Concen-
tration
(mg/L)
(mg/L)
(mg/L)
(pg/L)
(mg/L)
(mg/li)
(pg/L)
( jg/L)
(mg/L)
(iig/L)
(pg/L)
(mg/L)
(mg/L)
(mg/L)
(mg/L)
REFERENCES
Tollefson (1977),
Amberg (1977)
Amberg (1977)
Ainberg (1977)
Strachila & Ilamlin
(1977), Strachila (1.97
Strachila & Hamlin
(1977), Amberg (1977)
Tollefson (1977)
Strachila & Hamlin
(1977), Strachila (197
Strachila & Hamlin
(1977)
Strachila & Hamlin
(1977)
Ainberg (1977), Stra-
chila & Hamlin (1977)
Strachila (1978)
To]]ef son (1977)
Strachila & Hamlin
(1977)
Tollefson (1977)
Tollef son (1977),
Aniberg (1977)
Tollefson (1977),
Amberg (1977)
Amberg (1977)
CHEMICAL
22) Potassium
an e
CHEMICAL CONCENTRATIONS
Range
x
CROWN ZELLERBACH (MECHANICAL)
ITT-RAYONIER_(SULFITE)
10 Influent
10 Effluent
2° Effluent
10 Influenl
10 Effluent 2° Effluent
Range
23)
24)
25)
Ammonia-N
Xje lda l-N
Selenium
x
Range
x
Range
x
Range
x
26) Sodium
27) Thallium
Tin
29) Titanium
30) Zinc
31) Chloride
32) Sulfate
33) Sulfite
4.4
0.53
1.32
17.9
7789
69.9
63.7
80
2.3
L0.2—12.3
<5—20
270—300
12—41
20—95
).16—0.69
15-94
273—283
11.2
<11
285
150
15.5
57.5
0.42
63
278
150
40
60
150
150
40
Tr.
34) Sulfide (mg/L)
0.12

-------
Table 11-6. Continued, page 7
CHEMICAL CONCENTRATIONS -
CHEMICAL
OTHER
Defoaming Agents:
1) Nalco-129
Slimicide:
1) cytox R
Dyes:
1) Calcozine
(.aJ F-200 Yellow
Total Organic
Carbon
Color
(mg/L)
(mg/L)
(mg/L)
(mg/L)
(mg/L)
(1975)
Strachila & Hamlin
(1977)
Strachila & Hamlin
(1977)
mberg (1977)
Concen-
tration
anqe
ic Range R
CROWN ZELLERBACH (MECHANICAL)
ITT-RAYONIER_(SULFITE)
L° Influent
10 Effluent
2° Effluent
1° Influenl
10 Effluent
2° Eff
Range
tange Ic
Range
x
Range
x
REFERENCES
5.0
8.9
18.7
Young (1975)
Young (1975)
Young
625—755
960—4870
690
3451
Oil & Grease (mg/L)
1.4

-------
Table 11-7. CONCENTRATIONS OF OTHER PACIFIC NORTHWEST PULP AND PAPER MILL CONSTITUENTS
CHEMICAL
Range
CHEMICAL CONCENTRATIONS (mg/L)
range R
Range
MECHANICAL PULPING MILLS
SULFITE MILLS
10 Influent °Ef fluent 2 0 Effluent
10 Influent
10 Effluent
2 Eff3’ ent
Range
x
Range
Range
R
REFERENCES
FATTY ACIDS
1) Linolenic Acid
2) Linoleic Acid
3) Oleic Acid
4) Epoxystearic Acid
5) Dichiorostearic Acid
PHENOLS
I-a
1) Trichloroguaiacol
2) Tetrachloroguaiacol
RESIN ACIDS
1) Abietic Acid
2) DehydroabietiC Acid
3) Isopimaric Acid
0.02—0.1:
0.02—0.12
0.04—0.20
0.13—0.43
2.06—2.92
0.06—0.11
<0.02
0.07
0.12
<0.04
<0.04
<0.04
<0.04
0.28
67.4
51.8
2.48
8.7
0.09
<0.02
0.04
0.08
<0.04
<0.04
<0.04
<0.04
0.06
1.36
0.05
0.02-0.06
0. 02-0. 14
:0.02-0.10
1.00—1. 72
:0.02-0.08
3.2—16.0 !.
‘ .6—16.0
5.4—22.9
‘.7—35.0
1—5.9
:0.02
:0.02
0.07
:0.04
:0.04
0.04
:0.04
:0.02
:0.02
:0.02
Easty
(1978)
Easty et al.
(1978)
Easty et al.
(1978)
Easty et eL
(1978)
Easty et al.
(1978)
Easty et al.
(1978)
Easty et al.
(1978)
Leach & Thakor
(1975), Easty
et al.(1978)
Leach & Thakor
(1977)
Leach & Thakor
(1977),
Easty et al.
(1978)
Leach & Thakor
(1977)
Leach & Thakor
(1975), Easty
et al. (1978)

-------
Table 11-7. Continued, page 2
CHEMICAL
RESIN ACIDS (Cont.)
4) Pimaric Acid
CHEMICAL CONCENTRATIONS (mg/L)
.006—0.023 0.145
0.057—0.127
Leach & Thakor
(1977)
Easty et al.
(1978)
Easty et al.
(1978)
Easty et al.
(1978)
Leach & Thakor
(1977)
anqe
Range Range
MECHANICAL PULPING MILLS
SULFITE MILLS
10 Influent
L 0 Effluent 2°Effluent
1° Influent
1° Effluent
2° Effluent
x
Range
x
Ranqe
x
<0.1—5.9
2.8—7.7
Range
5) Dichlorodehydroa-
bietic Acid
6) Monochiorodehydro-
abietic Acid
7) Palustric Acid
OTHER
REFERENCES
0 06-0.09
<0.04—0.48
9.8
0.75 <0.02—0.03
(0.04
0.04 <0.04—0.48
0.02
<0.04
0.04
0.092
:0.02
:0.04
:0.04
L309
L007-
LOll
Easty et al.
(1978)
1) Chloroform

-------
secondary treatment is in direct contrast with other research-
ers. According to Easty, et al. (1978), this toxin is degraded
in secondary treatment.
In the case of heavy metals, aluminum, mercury, and zinc con-
centrations appear to be quite high (7,686 u/i for zinc) in
Crown Zellerbach effluent preceeding 1977 (Amberg, letter of
June 16, 1977). It should be noted that Crown Zellerbach had
switched from zinc hydrosuif its to sodium hydrosu].fite in 1977
thus reducing zinc concentrations greatly, to as little as 70
parts per billion (ppb) (Watkins, letter of December 13, 1977)
Crown Zellerbach mercury concentrations (0.5 ug/]. were moder-
ately high (Ainberg, letter of June 16, 1977). ITT Rayonier
mercury concentrations were reported as 0.1 — 0.2 ugh. The
reason for considerably higher Crown Zellerbach mercury concen-
trations could be due to the fact that recycled newsprint mills
discharge more mercury than do sulfite mills (Britt 1970).
Recently, ITT Rayonier expanded its monitoring program to
include the “Priority Pollutants” of concern to EPA. Monitor-
ing was conducted both prior to and subsequent to secondary
treatment installation. Data prior to installation of second-
ary treatment (1978 data) is included in Table 11—6 and agrees
with the pre—1978 ranges and average values except in a few
cases (mostly metals). Post secondary treatment data is shown
for both influent and effluent of secondary treatment (Table
11-8). Phenols, most fatty acids and most resin acids are
greatly reduced by secondary treatment, sometimes by factors of
2 - 40 times. Two resin acids, isopiinaric and chlorodehydro-
abietic acid, show significant increases; however the fact that
these were not detected in the influent suggests that these may
136

-------
Table 11-8. PRIORITY POLLUTANT SAMPLING AT ITT RAYONIER
AFTER INSTALLATION OF SECONDARY TREATMENT (mg/i)
Source: Vasquez 1980
Compound
Secondary
Influent
Extended
Outfall
Effluent
Phenol
5
<1
2,4 dichlorophenol
5—12
4—7
2,4,6 trichloropheno].
15—67
13—26
Trichloroguiaco l
247
3—149
Tetrachloroguiacoi -
40
16-34
Dehydroabietic acid
205
7
Isopimaric acid
N/D*
20
Abietic acid
N/D
N/D
Linoleic acid
N/D
1
Oleic acid
6
7
Pimaric acid
N/D
N/D
Chiorodehydroabietic acid
N/D
5
*N/D means none detected and is considered by ITT Rayonier
data as equivelent to a zero reading.
137

-------
be breakdown products of other toxicants in the secondary
treatment process.
Thus, Crown Zellerbach’s organics and inorganics testing was
quite limited. ITT Rayonier had described constituent con-
centrations better but still not as effectively as they could
have, especially the organics which are described as major
toxicants. The chronic and acute toxicants of these organics
can be found in Chapter V.
138

-------
REFERENCES
CHAPTER II
Amberg, H.R. June 16, 1977. Letter to D. Tight.
Application No. 071—OYB—2—000135. June 20, 1971. For Waste
Discharge Permit, submitted by Atlantic Richfield Co.,
Port Angeles, to U.S. Army Corps of Engineers.
Application No. WA—002397—3. September 26, 1973. For NPDES Waste
Discharge Permit, submitted by City of Port Angeles to
EPA and DOE.
Application No. WA—003772-9. July 5, 1974. For NPDES Waste
Discharge Permit, submitted by Pres—Sure-Matic, Inc. to
- EPA and DOE.
Application No. WA—003784-2. September 2, 1974. For NPDES
Waste Discharge Permit, submitted by M & R Timber, Inc. to
EPA and DOE.
Application No. WA—003805—9. December 20, 1974. For NPDES
Waste Discharge Permit, submitted by Peninsula Plywood Corp.
to EPA and DOE.
Application No. WA—003833-4. January 20, 1975. For NPDES Waste
Discharge Permit, submitted by Washington State Department
of Fisheries to EPA and DOE.
Berner, P.A. January 21, 1976. Letter to DOE, St. Martin’s
College, Olympia, Washington.
Britt, Kenneth (ed.). 1970. Handbook of Pulp and Paper Tech-
nology . Van Nostrand Reinhold Company. New York. 7 3 pp.
Clemetson, Thomas 0. September 1967. Limitations of the PBI
Analysis for Sulfite Liquor Measurement and the Data
Interpretation. Unpublished report.
Discharge Monitoring Reports. September 1972, January 1973 and
January 1975. Submitted by ITT Rayonier, Inc., Port Angeles
to DOE.
Discharge Monitoring Report. November 1970. Submitted by
Fibreboard Corporation, Port Angeles to WPCC.
Easty, D.B., L.G. Borchardt, and B.A. Wabers. 1978. Removal of
Wood-derived Toxics from Pulping and Bleaching Wastes . En-
vironmental Techincal Series. EPA-600/2-78 --03l. 77 pp.
139

-------
ENCON. 1974. North Olympic Coastal Basin Water Quality Manage-
ment Plan and 303(e) Addendum. Basin No. 13-11-09, WRIA
17,18,19,20.
Felicetta, Vincent F. and Joseph L. McCarthy. June 1963. “Spent
Sulfite Liquor: x. The Pearl-Benson or Nitroso Method for
the Estimation of Spent Sulfite Liquor Concentration ifl
Waters.” TAPPI 46(6): 337—346.
Fenske, Fred. October 14, 1980. Personal communication to
Kathryn Pazera, Biologist, NEC.
Folson, M.W. and J.G. Denison. January 8, 1976. Port Angeles
Division Effluent: Cooperative Water Quality Study with
Washington State Department of Fisheries. Report, ITT
Rayonier, Inc. Olympic Research Division .
Greiling, Rich. August 8, 1978. Letter to Bub Olsen, Pres-
Sure—Matic, Inc., Port Angeles, Washington.
Helle, O.G. December 28, 1976. Letter to Stanley M. Springer,
District Engineer, DOE, Southwest Regional Office, Olympia,
Washington.
Helle, O.G. June 30, 1977. Letter to Stanley M. Springer, Dis-
trict Engineer, DOE, Southwest Regional Office, Olympia,
Washington.
Hemingway, R.W. and H. Greaves. 1973. “Biodegradation of
Resin Acids and Sodium Salt.” TAPPI 56 (12): 189—192.
Kendall, J.U. November 24, 1971. Letter to Jim Knudson, DOE,
Olympia, Washington.
Leach, J.M. and A.N. Thakore. 1975. Toxic Constituents in
Mechanical Pulping Effluents. International Mechanical
Pulping Conference. June 16—20, 1975. San Francisco,
California.
Leach, J.M., J.C. Mueller, and C.C. Walden. 1976. “Identifica-
tion and Removal of Toxic Materials from Kraft and Ground-
wood Pulp Mill Effluent.” Process Biochemistry . January -
February, 1976.
Leach. J.M. and A.N. Thakore. 1977. “Compounds Toxic to Fish
In Pulp Mill Waste Streams.” Prog. Water Tech . 9: 787—798.
Monahan, Frank and Rick Pierce. August 11, 1980. Personal
Communication to Kathryn Pazera, Biologist, NEC.
Mueller, J.C., J.M. Leach and C.C. Walden. 1977. “Detoxifica-
tion of Bleached Kraft Mill Effluents - A Manageable Pro-
blem.” TAPPI Environmental Conference. April 25—27, 1977.
Chicago, Illinois. P. 72—124.
140

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Olsen, E.V. August 22, 1974. Letter to DOE, Southwest Washing-
ton Regional Office, Olympia, Washington.
Olympic National Park Service Personnel, United States Depart-
ment of the Interior. 1979. Personal Communication to
Kathy Pazera, Biologist, NEC.
Owens, J.M. September 16, 1975. Letter to M & R Timber, Inc.,
Port Angeles, Washington.
Permit No. WA—002427—9. April 17, 1974. NPDES Waste Discharge
Permit issued by EPA to Department of Transportation,Coast
Guard, Port Angeles Air Station.
Permit No. WA—000079—8. August 30, 1974. NPDES Waste Dis-
charge Permit issued by DOE to ITT Rayonier, Inc., Port
Angeles. Incorporates modifications of January 24, 1975,
October 22, 1975 and March 1, 1977.
Permit No. WA—002397—3. September 3, 1974. NPDES Waste Dis-
charge Permit issued by DOE to City of Port Angeles.
Permit No. WA—002446—5. December 30, 1974. NPDES Waste Dis-
charge Permit issued by EPA to U.S. Department of the
Interior, National Park Service, Olympic National Park.
Permit No. WA—000292—5. December 31, 1974. NPDES Waste Dis-
charge Permit issued by DOE to Crown Zellerbach Corp., Port
Angeles. Incorporates modifications of April 28, 1977.
Permit NO. WA-003805—9. July 9, 1975. NPDES Waste Discharge
Permit issued by DOE to Peninsula Plywood Corp., Port
Angeles, Washington.
Permit No. WA—000l42-2. July 23, 1975. NPDES Waste Discharge
Permit issued by DOE to Atlantic Richfield Company, Port
Angeles, Washington.
Permit No. WA—003833—4. September 4, 1975. NPDES Waste Dis-
charge Permit issued by DOE to Washington State Department
of Fisheries for Dungeness Salmon Hatchery.
Permit No. WA-003803- 2 . September 4, 1975. NPDES Waste Discharge
Permit issued by DOE to Washington State Department of
Fisheries for Elwha Salmon Channel.
Robinson, Ron. Ocotober 14, 1980. Personal communication to
Kathryn Pazera, Biologist, NEC.
Rock, Chet. April 4, 1979. Personal communication to Kathy
Pazera, Biologist, NEC.
141

-------
Springer, S. May 23, 1977. DOE Inspection Report of Penin-
sula Plywood Corporation, Port Angeles, Washington,
Springer, Stan. July 26, 1977. Letter to Lloyd Taylor, DOE,
Olympia, Washington.
Stolz, F.W. February 10, 1975. Letter to James P. Behlke,
Executive Assistant Director, DOE, Olympia, Washington.
Strachila, R. July 28, 1978. “Priority Pollutant Metal
Analyses in Port Angeles Feed Water and Effluent.”
Research Communication, ITT Rayonier, Inc., Olympic Re-
search Division. Project 122:145 file H 10:2—3.
Strachila, R.L. and Phil A. Hamlin. December 15, 1977. Letter
to FE. Royce, ITT Rayonier Inc., Port Angeles Division, WA.
Stroble, R.E. March 24, 1976. Letter to DOE, Olympia, Washing-
ton.
Tol].efson, Roger. June 29, 1977. Letter to John McChord, ITT
Rayonier Inc., Port Angeles, Washington.
United States Environmental Protection Agency. No Date.
Engineering Evaluation Report on the Application for a
NPDES Permit for U.S.D.I,, National Park Service, Olympic
National Park, Heart 0’ the Hills Campground.
Vazquez, M.A. April 1, 1980. “Analysis of Port Angeles Divi-
sion Effluent for Extractable Priority Pollutants: First
Sampling Program. ” Research Communication, ITT Rayonier,
Inc., Olympic Research Division. Project 122:161 file H
10:2—7.
Washington State Department of Ecology. 1974. Evaluation of
Application No. WA 003784—2, M & R Timber, Port Angeles,
Washington.
Washington State Department of Ecology. May 5, 1977. Evalua-
tion of Application No. WA-002397—3, city of Port Angeles,
Sewage Treatment Plant, Port Angeles, Washington.
Washington State Department of Ecology (a). No Date. Fact
Sheet — Technical Information on Application No. WA—003803—2,
Washington Department of Fisheries, Elwha Salmon Channel.
Washington State Department of Ecology (b). No Date. Fact
Sheet - Technical Information on Application No. WA-003833—4,
Washington Department of Fisheries, Dungeness Salmon
Hatchery.
142

-------
Washington State Department of Ecology (c). No Date. Evalua-
tion of Application No. WA-003772—9, Pres—Sure—Matic, Inc.,
Port Angeles, Washington.
Washington State Department of Ecology (d). No Date. Evalua-
tion of Application No. WA—00279—8, City of Port Angeles,
Port Angeles Car Wash, Port Angeles, Washington.
Washington State Department of Ecology (e). No Date. Fact
Sheet — Technical Information of Application No. WA—
002397—3, City of Port Angeles, Sewage Treatment Plant,
Port Angeles, Washington.
Washington State Department of Ecology. No Date. Water Pol-
lution Abatement and Water Quality Improvement in Port
Angeles Harbor. Located in DOE files, Southwest Regional
Office, Olympia, Washington.
Walden, C.C. and T.E. Howard. 1976. The Toxicity of Pulp and
Paper Mill Effluents and corresponaing Measurement Pro-
cιdures . Water Research 10 (8): 122—125.
Watkins, S.K. December 13, 1977. Letter to J.F. Cormack,
Environmental Services Division, Supervisor, Water Pro-
grams, Crown Zellerbach Corp., Port Angeles, Washington.
Wood, Dean. August 1]. and 14, 1980. Personal communication
to Kathryn Pazera, Biologist, NEC.
Wood, Dean. October 10, 1980. Personal communication to Kathryn
Pazera, Biologist, NEC.
Young, S.R. February 14, 1975. Port Angeles Effluent Fish
Bioassays, Crown Zellerbach Research Memorandum No.
176—179. Crown Zellerbach Corp., Port Angeles, Washington.
143

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III. OCEANOGRAPHIC DYNA MICS
The objective of this chapter is to describe the distribution
and dilution of effluent from the two active pulpmills at
Port Angeles in the marine receiving waters. This objective
will be met by first briefly reviewing existing studies, second,
presenting base conditions of the marine environment, arid
finally, examining evidence pertaining to dynamics of the physi-
cal system and the behavior of pulp effluent within it.
Confirmation studies of these oceanographic conditions have
recently been conducted both in the field and on a hydraulic model
of Strait of Juan de Fuca by Ebbesineyer et al. (1980) and are
reported in Chapter VIII. Implications of dispersion and dilu-
tion patterns on water quality, toxicity and other effects on
biological organisms are discussed in appropriate sections of
Chapters VIII and Ix. For more detail see Ebbesmeyer et al. 1980.
The primary oceanographic study area coincides with those used
for other aspects of this study and extends from the Elwha
River to Dungeness Spit (see Figures 1 1 1—i and 111—2 ). Analysis
of that area presented in this and later chapters utilizes field
observations of currents, winds and pulpmill effluent, supple—
merited by mathematical and theoretical calculations based on
standard oceanographic principals. Data were obtained from
municipal, state, federal and private institutions for the
period 1932 — 1980. These include field data as well as informa-
tion derived from numerical and hydraulic models. Additional
field observations of suspended sediment, oil spills and cer-
tain constituents of pulprnill effluent were used as traces
of water movement. Previous literature and data bases are dis-
cussed in Section 111—A below.
A. EXISTING LITERATURE AND DATA
Descriptions of certain aspects of the dispersion of pulp mill
effluents discharged to marine waters in or near the Harbor have
144

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• VANCOUVER
1SLAND’ .
.•
BRITISH
COLUMBIA
PACIFIC
OCEAN
AN ELE
HA RB OR
NGTON
• ••,•
• • .
1. . . . •
S H
I •. ••
145

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I 24
123 W
r
Figure 111-2. EXPANDED VIEW OF STUDY AREA AND
APPROACHES
Notation: Hatched lines,
sills; G-V sill, Green
Point-Victoria sill; CGAS,
Coast Guard Air Station;
and dashed line in inset,
proposed submarine petro—
leum pipelines.
14.6

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previously been given by several investigators including
Stein and Denison (1966), the Washington Pollution Control
Commission (1967), Bartsch et al. (.1967), Tollefson et al.
(1971), and the U.S. Environmental Protection Agency (1974)
These reports tended to concentrate only on effluent from ITT
Rayonier and only two (Tollefson et al., 1971; EPA 1974) des-
cribe the dispersion of ITT Rayonier’s effluent away from its
present discharge location. This chapter and Section VIII-A
give the basis for combining the results of earlier reports
with recent oceanographic data to create a more complete pic-
ture of the dispersion of both ITT Rayonier and Crown Zeller-
bach wastes from their present discharge locations.
1. Tides
The National Ocean Survey (hereafter NOS) has published pre-
dictions of the tides at several locations throughout the
study area based on short term tide r easurements taken during
the early 1960’s. In general we have used predictions of the
tides at the eastern end of Ediz Hook. The mean tide range
(at Ediz Hook 1.3 m) is defined as the difference in height
between mean high water and mean low water. The diurnal range
(2.2 m) is the difference in height between mean higher high
water and mean lower low water (NOS 1980a).
Tidal harmonics based upon recent measurements have been re-
ported by Parker (1977) for tide stations throughout the Strait
of Juan de Fuca.
2. Currents
Currents have been measured at many stations in the Strait of
Juan de Fuca using both moored and over the side current
meters. Summaries of these observatons are listed in Appendix II
A. Early measurements were taken by the U.S. Coast and Geode-
tic Survey (USCGS) in 1963 - 1964 using Roberts current meters.
147

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These measurements were usually less than five days in
length and provide the basis of many tidal current
predictions (NOS 1980b).
More recent measurements were taken by and obtained from
the NOS and the Pacific Marine Environmental Laboratory
(PMEL) of the National Oceanic and Atmospheric Administration
(NOAA). These measurements were made with Anderaa and vector
averaging current meters (VACM) for periods of 15 days or
longer. The current meters were usually deployed at 5 in depth
below the water surface, mid-depth, and 15 in above the bottom.
Other measurements near the mouth of the Harbor have been
taken by ITT Rayonier, EPA and Tollefson et al. (l97lL Some
aspects of these data have been previously presented by Tollef-
son et al. (1971) , NOS (1976) , Parker (1977) , Cannon (1978)
Holbrook and Halpern (1977), Ebbesmeyer et al. (1979), and Hol-
brook et a].. (1980). Original records were obtained from NOS
in Rockville, Maryland and PMEL in Seattle, Washington.
Currents have also been measured by tracking the movements of
several drifting objects: drogues tethered at selected depths,
thin flexible plastic sheets, and small plastic cards. Drogue
movements during several one-hour periods have been reported by
Charne].l (1958), Tollefson et al. (1971), EPA (1974), and Ebbes—
meyer et a]. (1978). The trajectories of several hundred drift
sheets were obtained by Ebbesmeyer et a].. (1978) and Cox et a]..
(1978) in the study area during daylight using a small aircraft.
Recoveries onshore of several thousand drift cards released in
the Harbor and its approaches have been tabulated by Ebbes—
meyer et al. (1978) and Pashinski and Charnel]. (1979).
Currents have also been measured using a high frequency radar
system (Frisch 1980; Frisch and Holbrook 1980). This system senses
148

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currents in the upper ½ m of the water column and has been
described by Barrick et al. (1977). The results were averaged
onto a grid with a spacing of 1.3 km. The measurements were
made continuously for two one-week periods in 1978 and 1979.
3. Water Properties
Prior to the introduction of modern electronic field equip-
ment, water properties were taken throughout Puget Sound and
the Strait of Juan de Fuca by the University of Washington
and Canadian institutions at rather widely spaced stations.
These measurements disregarded tide stage. These stations
have been tabulated through 1966 by Collias (1970). Tempera-
ture, salinity, and dissolved o cygen commonly have been sampled
at mid—channel monthly during selected years since 1932.
Recently many coordinated measurements of water properties
and currents have been made in the Strait of Juan de Fuca pri-
marily by NOAA and EPA. Currents have been recorded several
times per hour for periods lasting months and conductivity—
temperature—pressure (CTD) systems have been used to provide
closely spaced data on vertical profiles. These observations
have been partially summarized by Cannon (1978) and Holbrook
et al. (1980).
In the Harbor and close approaches a number of surveys have
been conducted since 1950, at intermittent periods and lasting
several days or less (Appendix Ill-B). Durinq 1963 - 1964. monthly
surveys consisting of approximately a dozen stations inside the
Harbor and a reference station located approximately 2 km
north of the tip of Ediz Hook were taken (Callaway et a].. 1965).
These surveys have been described by Bartsh et a].. (1967) and
contours of these data are presented in Appendix Ill—C.
149

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4. Winds
Seasonal. patterns of prevailing winds over the Strait of Juan
de Fuca nave been diagrammed by Harris and Rattray (1954).
Atmospheric conditions associated with these winds have been
explained by Phillips (1966) , Maunder (1968) , Nelson (1977)
Lilly (1978), Holbrook and Halpern (1978), Cannon (1978),
Overland and Vimont (1979), and Holbrook et al. (1980). Winds
have been computed for the area by Overland et al. (1978)
using a numerical model: their results have been summarized by
Cannon (1978)
Mean hourly wind speed and direction at the U.S. Coast Guard
Air Station on Ediz Hook have been tabulated based on observa-
tions during 1948 - 1953 by the U.S. Department of Commerce
(1973). Summaries of this data have been presented by EPA
(1974). Mean wind speed by hour at Port Angeles during 1947 -
1952 has been tabulated by the Pacific Northwest River Basin
Commission (1969) - Additional summaries of wind data at Port
Angeles have been presented by the U.S. Department of Agricul-
ture (1936) and the University of Washington (1953).
Winds were also measured over the water by Callaway et al. (1965)
during observations of water properties. Hourly wind data taken
at the U.S. Coast Guard Air Station just prior to and during
these and other hydrographic surveys were obtained for this
report from the National Climatic Center in Asheville, North
Carolina.
5. Air Temperature and Precipitation
Summaries of monthly average air temperature and precipitation
for Port Angeles have been presented by the University of Wash-
ington (1953) based on data from 1910 - 1940, and by the U.S.
150

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Department of Commerce (climatoJ.ogica]. summary) compiled
from data during 1931 1960 (U.S. Department of Commerce 1973).
6. Runoff
Monthly average river discharge data were obtained for the
Elwha River (1961 — 1970), Dungeness River (1961 — 1970) from
the U.S. Geological Survey (1971, 1974). The 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.
7. Suspended Sediments
At times there are significant amounts of sediment contained
in the local runoff. Sediment input to the marine waters from
the Elwha River and erosion of the cliffs west of Ediz Hook
have been estimated by the U.S. Army Corps of Engineers (1971).
8. Aerial Photographs
Aerial photographs of the study area were obtained from several
sources as listed in Appendix III-D. Photographs were examined for
patterns of suspended sediment, pulp mill effluent, and surface
temperature.
9. Oil Spills
In 1971 approximately 880 m 3 ( 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
151

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University of Washington. Description of the probable oil
movement at depth was obtained from Professor Clifford A.
Barnes (letter of November 26. 1974) as reported by
Ebbesmeyer et al. (1979).
On May 13, 1979 at 1020 (Pacific Daylight Time (PDT)) approxi-
mately 2.3 m 3 ( 600 gallons) of Number 4 fuel oil was spilled
from the commercial vessel ATLANTIC HORIZON at the mouth of
the Harbor. Data on the spill’s dispersion were collected
in the form of photographs on May 14 between 1400 — 1500 by
personnel from NOAA and Evans—Hamilton, Inc. (EHI). The
photographs were taken from a small aircraft at approximately
300 m altitude.
10. Hydraulic Tidal Model
The field data were supplemented by observations of water and
dye movement in a hydraulic tidal model of the eastern Strait
of Juan de Fuca (Figure 111—3). The model was constructed by
personnel of E}II, and has been described by Ebbesuteyer et al.
(1979)
Water movement in the model was determined from streak photo-
graphs taken as follows:
1) the water in the model was dyed with black (India)
ink and the surface was sprinkled with bronze dust;
2) the shutter interval of a camera mounted overhead
was set at one second (approximately 35 minutes in
the prototype) with the result that movements of
the dust particles on the water surface appeared as
streaks in the photographs;
3) streak photographs were taken at short intervals
through a tidal day. Photographs were obtained with
the tide generating machine set to approximate
spring tides.
Similar techniques have been used by Collias et al. (1973) and
McGary and Lincoln (1977) to obtain patterns of tidal currents
in the hydraulic tidal model of Puget Sound.
152

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I
I
I
DECEPTION
PASS
O.36 *
1.O9
T
I
I
-
Figure 111-3. SCHEMATIC OF THE HYDRAULIC TIDAL MODEL
153

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Dye movement in the model was determined from sequential
photographs taken at one second intervals through a tidal
day. Comparisons both of streak and dye photographs with
field observations have been presented by Ebbesmeyer et al.
(1979) as partial verification of the model.
B. PHYSICAL SETTING
The physical elements which influence the marine environment
include adjacent bathymetry geography (affecting river runoff),
winds and general climate. Other physical factors involving
water characteristics are discussed in Chapter IV.
1. Geography
The study area encompasses a variety of prominent geographical
features. The inner Strait of Juan de Fuca has bathymetry that
is highly irregular consisting of a complex of channels and
banks (Figure 111-4). Shallowest depths may be traced from
the U.S. shore between Green Point and Dungeness Spit to the
Canadian shore on Vancouver Island. This sill has an average
depth of approximately 60 m and greatest depth of 115 m which
is offset from mid-channel toward the south. For clarity this
sill will be referred to as the Green Point — Victoria sill.
At the western edge of the study area there is a lateral con-
striction of the Strait of Juan de Fuca. It is bounded by
submarine projections of Vancouver Island on the north and of
the Elwha River delta on the south (Figure 111-4). At this
cross section the mid—channel depth is approximately 210 m.
The characteristic dimensions of the Harbor have been summarized
in Table 111—1 based on a recent bathymetric chart (No. 18468,
dated May 22, 1976). At the Harbor’s mouth there is a sill—like
feature (approximately 44 in depth); westward the Harbor depths
154

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L2e 27 26 123’25 24
igure 111-4. BATHYMETRY (FATHOMS) WITHIN THE STUDY
AREA (TOP) AND PORT ANGELES HARBOR
(BOTTOM)
Notation: hatched lines, Green Point-Victoria sill. (top) and
Harbor entrance sill-like feature (bottom); dashed lines,
lateral constriction of the Strait of Juan de Fuca.
Conversion factor: 1 fathom — l.83m
155
35.
25
O i2!
r 2e
27
26
t2 ’ 2
2’
23

-------
Table Il l-i. CHARACTERISTIC DIMENSIONS AND RATIOS
OF PORT ANGELES HARBOR*
Dimensions
X io 6
units
1. Volume below mean lower low water
209.
m 3
2. Volume between mean lower low
20.7
m 3
and mean higher high waters
3. Harbor area at mean lower low
9.31
m 2
water
4. Cross sectional area of Harbor
0.0519
m 2
entrance
5. Harbor length, entrance to head
0.00444
m
Ratios
X
units
1. Bulk residence period = Volume (1)!
Tidal prism (2)
10.1
tidal
cycles
2. Characteristic tidal speed = tidal
prism (2)/cross sectional area (4)1
quarter tidal day
0.0177
m
* West of 1230 24’W longitude
156

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increase to approximately 59 m (Figure 111—4). The entrap-
ment interval between sill and basin depths is approximately
15 m. The surface area of the Harbor is approximately 9 kin 2 ,
equivalent to about 0.6% of the surface area of the inner
Strait of Juan de Fuca.
The topography within the study area (Figure 111—5) has sig-
nificant relief. To the south the Olympic Mountains form
a ridge oriented approximately southeast - northeast. Fairly
level land of low elevation borders the water.
Some of man’s activities in the area have drastically reduced
the amount of sediment transported alongshore that is necessary
to maintain the configuration of Ediz Hook (see Pacific North-
west Sea, 1974). Prior to 1930 there were two major sources
of sediment: the Elwha River and the cliffs between the Elwha
River and Ediz Hook. In 1910 - 1911 and 1925 — 1928 dams were
constructed on the Elwha River and in 1930 a water supply line
and rock covering were constructed along the base of the cliffs.
It has been estimated that the dams and rock covering together
resulted in about a 75% decrease in the sediment that nourishes
Ediz Hook. Since these projects were completed Ediz Hook has
significantly eroded (U.S. Army Corps of Engineers 1971) and a
number of attempts have been made to stabilize its present
shape. In the event that the shape is significantly changed
some of the present results may no longer be applicable.
2. Climate
Figure 111—6 shows the seasonal cycles of air temperature and
precipitation at Port Angeles and runoff from local rivers and
creeks as well as the Skagit and Fraser rivers, the major
sources of freshwater entering Puget Sound and Strait of Georgia,
respectively. Port Angeles has relatively moderate temperatures
157

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Figure 111-5. TOPOGRAPHY (METERS) WITHIN THE STUDY AREA

-------
a) AIR TEMPERATURE
‘4
12
10
a
S
4
2
.1 M*M J 1£ 5ON 0 J
c) LOCAL RUNOFF
b) PRECIPITAION
d) OTHER MAJOR RUNOFF
I’
o 4
z
I-.
w
U) 2
MONTHS
M A N J ‘A $ ‘0 N 0
Figure 111—6
SEASONAL CYCLES OF LOCAL A) AIR TEMPERATURE,
B) PRECIPITATION AND C) RUNOFF. THE SKAGIT
AND FRASER RIVERS COMPRISE D) OTHER MAJOR
RUNOFF
- 1960
/
I
V
55
.
50
I
U
w —
45 0 .
0
Li
I .-
40
Li
0.
35
YEARS UNKNOWN
U
.
Li
Li
0.
Li
I -.
4
0
0
z
z
S
z
0
I-
0.
U
LI
a.
2
U.
0
I
Li
4
I
U.
159

-------
throughout the year due to the presence of the warm Jap-
anese current flowing southward off the coast o Washing-
ton. Precipitation at Port Angeles averages 49.5 cm per
year (Holbrook et al. 1980) with lowest values occurring
during July and August and highest values during winter.
The majority of this precipitation enters the marine waters
as river runoff. Annually, approximately 40 km 3 and 150
km 3 of freshwater are discharged into Puget Sound and the
Strait of Georgia, respectively; whereas rivers and creeks
near Port Angeles discharge 2 kin 3 . Seasonally, runoff is
modified by the winter snowpack at high altitudes. Most
major rivers draining mountainous regions such as the Fraser
River reach their maximum discharge during early summer when
spring thawing occurs. Those draining both lowlands and
mountainous regions such as the Skagtt River (entering Puget
Sound) and the Elwha River, Dungeness River, and Morse Creek
near Port Angeles have maximum discharges during both winter
and summer (Figure 111-6). Siebert Creek drains primarily
lowlands and therefore reaches its maximum discharge in winter
when precipitation is highest.
3. Winds
The seasonal progression of prevailing winds over western
Washington has been previously presented by Harris and Rat—
tray (1954). They indicate that throughout the year winds
in the study area are typically from the west (Figure 111—7).
The relative frequency and strength of these westerly winds to
those from other directions have been calculated from a sum-
mary (Pacific Northwest River Basin Commission 1969) of six
years (1948 - 1953) of hourly winds at the Coast Guard Air
Station near the tip of Ediz Hook. Westerly winds are dom-
inant from March through October. Winds are more evenly divid-
ed in direction during the remainder of the year, generally
160

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Figure 111-7 . SEASONAL PROGRESSION OF PREVAILING
WINDS
Adapted from Harris and Rattray, 1954
161

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with no dominant direction (Figure III—8a). On an annual
basis 55% of the winds are from the southwest to northwest
fluctuating between a January minimum of 32% and a July
maximum of 86% (Figure III—8b). Winds are calm during 7%
of the year.
Highest wind speeds are also generally from the west except
during December and January when they are matched occasion-
ally by winds out of the north to northeast (Figure Il l—Bc).
Wind speeds from the west average between 5 and 6 m sec 1
with maximum speeds occurring in April and May.
The winds at Port Angeles exhibit a pronounced seabreeze
occurring in late afternoon during the months of April
through August (Figure III—8d). Cannon (1978) has also noted
this seabreeze effect. The seabreeze is typified by average
wind speeds from 2 - 4 in sec at night, increasing winds
around noon reaching average speeds of 6 m sec at approxi-
mately 1800, then decreasing at midnight.
C. DYNAMICS
The dynamics of the waters near Port Angeles are governed by
tides, strearnf low, wind, corio].is force and other physical
factors. The influence of these forces produces directional
currents, tidal eddies, vertical mixing and other water move-
ments characteristic of the study area. Some of these water
movements illustrate general oceanographic principals, while
others are unique to the area, resulting from the particular
forces, shoreline and bottom configuration at Port Angeles.
In addition to movement of the water itself, the interaction
of mill effluent with the marine environment produces its own
important parameters. Indicators of environmental effects of
162

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a,
C)
0
I-
0
U,
).. .s
0
a
.3
MONTHS
Figure 111-8 . PERCENTAGE OF THE TIME THE WIND BLOWS FROM (A)
INDIVIDUAL AND (B) GROUPED DIRECTIONS (16 DIR-
ECTIONS TOTAL) DURING EACH MONTH, AND WIND SPEED
BY (C) DIRECTION, AND (D) HOUR OF THE DAY DURING
EACH MONTH
Source: U.S. Dept. of Commerce (1973), Pacific Northwest
River Basins Commission (1969)
0
I-
UJ
0
C)
.7
.5
163

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the effluents include residence time, dilution and dispersion
of the effluent (horizontally and vertically). Due to the
complex nature of these factors, they can only be deduced
following extensive analysis of the data. The specifics of
currents, eddies and effluent dynamics in the study area have
been deduced from considerable data analysis and modeling and
are discussed fully in Chapter VIII.
164

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CHAPTER III
Barnes, C.A. November 26, 1974. Letter to Washington
State Department of Ecology, Olympia, Washington.
Barrick, D.E., M.W. Evans, and B.L. Webber. 1977. “Ocean
Surface Currents mapped by Radar.” Science 198:4313.
Bartsch, A.F., R.J. Callaway, and R.A. Wagner. 1967. “Tech-
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Callaway, R.J., J.J. Viastelicia, and G.R. Ditsworth. 1965.
Unpublished data on file at the Environmental Protection
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Cannon, G.A. 1978. “Circulation in the Strait of Juan de
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Charnell, H.V. June 10, 1958. “ Jater Quality, Port Angeles
Harbor 1956—1958.” ITT Rayonier, Inc. Port Angeles,
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Co].lias, E.E. 1970. “Index to Physical and Chemical Oceano-
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Collias, E.E., C.A. Barnes, and J.H. Lincoln. 1973. “Skagit
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Cox, J.M., C.C. Ebbesmeyer, and J.M. Helseth. 1978. Surface
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Ebbesmeyer, C.C., and J.M. Cox, and J.M. Helseth. 1978.
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165

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Ebbesmeyer, C.C., J.M. Cox, and J.M. Helseth. November 1980.
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Holbrook, J.R., and D. Halpern. 1977. Observations of near-
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Holbrook, J.R., R.D. Muench, and G.A. Cannon. 1980. “Seasonal
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Lilly, K.E., Jr. 1978. “Northwest Washington Weather for the
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Lincoln, J.H. 1977. “Derivation of Freshwater Inflow Into
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Maunder, W.J. 1968. “Synoptic Weather Patterns in the Pacific
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National Ocean Survey. 1980a. “Tide Tables 1980.” U.S. Depart-
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166

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National Ocean Survey. 1980b. “Tidal Current Table 1980.”
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Nelson, C.S. 1977. “Wind Stress and Wind Stress Curl Over
the California Current.” NOAA Technical Report NWFS
SSRF -714, Washington, D.C. 87 pp.
Overland, J.E., M.H. Hitchman, and Y.J. Han. 1978. “A
Regional Surface Wind Model For Mountainous Coastal
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Overland, JE., and J.C. Vimont. 1979. “Marine Climatology
of Western Washington. IN: Puget Sound: Oceanography
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Volume 3, parts A and B.” PNRBC. Vancouver, Washington.
Pacific Northwest Sea. 1974. “The Hook.” Vol 7 (2), 4—14.
Parker, B.B. 1977. “Tidal Hydrodynamics in the Strait of Juan
de Fuca - Strait of Georgia.” National Oceanic and
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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.” NOAA Technical Memorandum ERL PMEL-14. 30 pp.
Phillips, E.L. 1966.”Washington Climate For These Countes,
Northeast Clallam, Northeast Jefferson, Island, San Juan,
Skagit, Snohomish, and Whatcom.” Cooperative Extension
Service, Washington State University, Pullman, Washing-
ton. 64 pp.
Stein, J.E., and J.G. Denison. 1966. “Port Angeles Water
Monitoring Program.” ITT Rayonier Olympic Research Div—
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Tollefson, R., J.G. Denison, and E. Tokar. August 30, 1971.
“Outfall Location Studies — Port Angeles, Washington.”
ITT Rayonier Olympic Research Division Report No. Hl0:1—3
Case 1230—16, Project 119:116. Port Angeles, Washington.
United States Army Corps of Engineers. 1971. “Report on Sur-
vey of Ediz Hook for Beach Erosion and Related Purposes,
Port Angeles, Washington.” Main report, Parts 1 and 2.
U.S. Army Corps of Engineers, Seattle District, Washington.
United States Department of Agriculture Weather Bureau. 1936.
“Climatic Summary of the United States.” Section 1 —
Western Washington. Government Printing Office, Washing-
ton D.C. 38 pp.
167

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United States Department of Commerce. 1973. “Cliinatological
Summary: Normals, Means and Extremes. Climatography of
the United States 20—45.” IN: U.S. Environmental
Protection Agency. 1974. aluation of ITT Rayonier,
Inc. Outfall, Port Angeles Harbor, Washington. National
Field Investigations Center Report No. EPA 330/3-74—001.
100 pp.
United States Environmental Protection Agency. 1974. “Eval-
uation of ITT Rayonier Inc. Outfall, Port Angeles Harbor,
Washington.” National Field Investigations Center Report
No. EPA 330/3—74—001. 100 pp.
United States Geological Survey. 1971. Surface Water Supply
of the United States 1961—65. Part 12, Vol. 1. Pacific
Slope Basins in Washington Except Columbia River Basin.
Water Supply Paper No. 1932. U.S. Government Printing
Office, Washington, D.C.
United States Geological Survey. 1974. Surface Water Supply
of the United States 1966—70. Part 12, Vol. 1. Pacific
Slope Basins in Washington Except Columbia River Basin.
Water Supply Paper No. 2132. U.S. Government Printing
Office, Washington, D.C.
University of Washington Department of Oceanography. 1953.
“Puget Sound and Approaches: A Literature Survey.”
Volume I: Climatology. Seattle, Washington. p.41-83.
Vagners, J., and P. Mar. 1972. “Oil On Puget Sound, An
Interdisciplinary Study in Systems Engineering.”
University of Washington Press, Seattle, Washington.
629 pp.
Waldichuk, M. 1957. “Physical Oceanography of the Strait of
Georgia, British Columbia.” Journal of the Fisheries
Research Board of Canada, 14, 321—486.
Washington State Pollution Control Commission. 1967. “Pollu-
tional Effects of Pulp and Paper Mill Wastes in Puget
Sound, a Report on Studies Conducted by the Washington
State Enforcement Project.” U.S. Department of the
Interior, Federal Water Pollution Control Administration.
474 pp.
Wedley, R.E. 1960. “A Summary of Recent Research by the
Washington State Department of Fisheries on the Distribu-
tion and Determination of Sulfite Waste Liquor (SWL). IN
Reports on Sulfite Waste Liquor in a Marine Environment and
Its Effect on Oyster Larvae . Washington State Department of
Fisheries Research Bulletin No. 6.
168

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IV. WATER QUALITY
The marine waters in the vicinity of Port Angeles are regulated
by both federal and state guidelines. National goals and guide-
lines are promulgated under the Federal Water Pollution Control
Act (P.L. 92-500) as amended by the Clean Water Act of 1977
(P.L. 95—217). The objectives of the act define six national
goals which are, in part:
• that the discharge of pollutants into navigable
waters be eliminated by 1985,
• that wherever attainable, an interim goal of water
quality which provides for the protection and the
propagation of fish, shellfish and wildlife, and
provides for recreation in and on the water be
achieved by July 1, 1983, and
• that the discharge of toxic pollutants in toxic
amounts be prohibited.
These goals are regulated by various federal agencies; however,
the U.S. Environmental Protection Agency (EPA) has regulatory
authority over industrial discharges administered through the
National Pollutant Discharge Elimination System (NPDES).
State regulatory control is defined by State Water Quality Stand-
ards as part of the Washington Administrative Code (WAC) (Chapter
173—201 WAC). These sections of the code:
• . are established in conformance with present and
potential water uses of (said) surface waters and in
consideration of the natural water quality potential
and limitations of the same.”
The Washington State Department of Ecology (DOE) first promulgated
and adopted Chapter 173-201 WAC on June 9, 1973 (DOE, Administra-
tive Order No. 73—4 filed July 8, 1973) and adopted permanent
amendments to the Chapter on November 16, 1973 (DOE; Administra-
tive Order No. DE 73-22 filed November 16, 1973) and again
on December 19, 1977 (DOE, Administrative Order No. DE 77—32,
filed January 17, 1978). DOE is responsible for the enforcement
of these State Water Quality Standards.
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Water quality studies presented in this section will utilize DOE
water quality parameters and standards as the main basis for
comparison. In order to provide an accurate comparison of
collected water quality data and state standards, previous
amendments to Chapter 173-201 WAC that differ from the present
water quality standards will be included in the text. Effluent
limitations and toxic substances are discussed in Chapters II
and V.
A. WATER QUALITY CRITERIA
The surface waters of Port Angeles Harbor (hereafter Harbor) and
the adjacent Strait of Juan de Fuca (hereafter Strait) are
classified by the State of Washington as Class A and AA surface
waters, respectively. The dividing line between these types
bears roughly south—southeast (true bearing 152°) from Buoy *2
at the tip of Ediz Hook (WAC 173-201—085(19)). The division
line is shown in Figure lI—i. The WAC 173—201—045 requires
Class AA surface waters (Extraordinary) to have the general
characteristics that:
“Water quality of this class shall markedly and uniformly
exceed the requirements for all or substantially all uses”
The characteristic uses for both categories of surface water (Class
A and AA) include, but are not limited to, the following:
• water supply (domestic, industrial, agricultural)
• wildlife habitat
• general recreational and aesthetic enjoyment
• navigation (and commerce for Class A)
• fish and shellfish reproduction, rearing and harvesting
while Class AA waters include the additional category of general
marine recreation. Those characteristic uses to be protected are
defined more fully for marine waters under WAC 173-201-050 which
is summarized for Class AA and Class A marine surface waters in
Table IV—l.
Washington Water Quality Criteria for Class AA and A surface
waters are shown, in part, in Table IV—2. Full statements of
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Table IV-1 CHARACTERISTIC USES TO BE PROTECTED UNDER
WAC 17 3-201-050 (CLASS AA AND A MARINE SURFACE WATERS)
Uses Water
Classification
AA
A
FISHERIES
Sa imonid
Migration
Rearing
Other Food Fish
Commercial Fishing
Shellfish
WILDLIFE
RECREATI ON
Marine (general)
Water Contact
Boating and Fishing
Environmental Aesthetics
WATER SUPPLY
Industrial
NAVIGATION
LOG STORAGE AND RAFTING
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Table IV-2. WATER QUALITY CRITERIA FOR CLASS AA AND CLASS A MARINE WATERS
(Extracted from 17 3—201—045 wAc) 1
Parameter Class AA Maximum, Minimum, Range or Variation Class A: Maximum, Minimum, Range or Variation
Fecal ηoliform 1) Shall not exceed median of 14 organisms 1) Shall not exceed median of 14 organisms per
organisms per 100 ml. 100 ml.
2) Not more than 10% of samples shall exceed 2) Not more than 10% of samples shall exceed
43 organisms per 100 ml. 43 organisms per 100 ml.
Total Coliform 1) Shall not exceed median of 70 organisms 1) Shall not exceed median of 70 organisms
organisms 2 per 100 ml. per 100 ml. 3
2) Not more than 10% of samples shall exeed 2) Not more than 20% of samples shall exceed
230 organisms per 100 ml when associated 1000 organisms per 100 ml when associated
with fecal source, with fecal source. 3
Dissolved Oxygen Shall exceed 7.0 mg/l. Shall exceed 6.0 mg/l.
Total Dissolved Shall not exceed 110% of saturation. Shall not exceed 110% of saturation.
Gas
Temperature 1) Not to exceed 13°C due to human activity. 1) Shall not exceed 16°C due to human activity.
2) When natural conditions exceed 13°C, no 2) When natural conditions exceed 13°C, no
temperature increase greater than 0.3 C temperature increase greater than 0.3 C
due to point sources. due to point sources.
pH 1) p11 shall range from 7.0 to 8.5. 1) pH shall range from 7.0 to 8.5.
2) Man—caused variations shall be < 0.2 units. 2) Man-caused variations shall be<0.2 units.
Induced variation shall be < .1 units. 2 Induced variation shall be < .25 units. 2
Turbidity 1) Not to exceed 5 NTU (when background 1) Not to exceed 5 NTU (when background
<50 NTU) < 50 NTU)
2) Not to exceed 10% above background (when 2) Not to exceed 10% above background (when
background >50 NTU) background >50 NTU)
Toxic, radioactive Shall not affect heath, natural aquatic Shall be below public health significance
or deleterious environment or desirability of water for or which may cause acute or chronic toxic
material and use, conditions to the aquatic biota or
adversely affect water use.
Aesthetic Values Shall not be impaired. Shall not be impaired.
1. Water Quality Standard contained in Chapter 173—201 WAC, adopted December 19, 1977, and filed January 17, 1978.
2. Water Quality Standards contained in Chapter 173-201 WAC, adopted June 19, 1973, and filed July 8, 1973.
3. Special conditions for Port Angeles Harbor only.

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these criteria can be found in WAC 173—201-030 (adopted June 19,
1973, filed July 8, 1973) and WAC 173—201—045 (adopted December 19,
1977, filed January 17, 1978)
State water quality criteria for specific parameters have under-
gone minor modifications since their initial adoption in 1973
(DOE, Administrative Order No. 73—4 filed July 8, 1973). The
main relevant changes have been a shift to less restrictive
ranges in man—induced pH change and total coliform organisms. The
1973 standards required the induced pH range to be less than 0.1
unit in Class A.A waters and less than 0.25 unit in Class A waters
(Table IV—2). According to the most recent revisions to Chapter
173-201- WAC (DOE, Administrative Order No. DE 77—22, filed
January 17, 1978), restrictions on fecal coliform organisms
replaced the water quality criteria on total coliform organisms
(Table IV—2).
Previous to June 19, 1973 water quality standards for the State
of Washington were divided into interstate and coastal water qual-
ity standards (Chapter 372 - 12 WAC) and interstate water quality
standards (Chapter 372 - 64 WAC). The water quality uses, criter-
ia and the specific classification areas for Port Angeles (Class
A and AA) from January 3, 1968 to June 19, 1973 resembled those
contained in Administrative Order No. 73-4 (filed July 8, 1973)
with the exception of pH and dissolved gases. The pH range for
both Class A and AA was restricted to 7.8 - 8.5 (WPCC, Docket No.
67-2 filed December 4, 1967 and DOE, Administrative Order No. 72-9
adopted and filed April 24, 1972. From December 1967
until June 18, 1973 there was no water quality standard for total
dissolved gas (Docket No. 67—2); however amendments (Administrative
Order No. 72-9) to the 1967 Water Quality Standards introduced
the dissolved nitrogen water quality criteria effective in the
Water Quality Standards from April 24, 1972 to June 18, 1973. In
both Class A and AA waters dissolved nitrogen concentrations were
not to exceed 110% of saturation at the sample point due to “non-
natural causes t ’. Washington Water Quality Standards effective
from February 29, 1960 until December 4, 1967 (WPCC, Rule .04.210
adopted February 29, 1960, filed March 1, 1960) did not designate
173

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specific areas of classification; therefore the same water qu ].ity
standards applied to all surface waters under the jurisdiction of
Washington state.
B. WATER QUALITY MONITORING
Port Angeles area water quality data derives from a varying group
of long-term water quality stations supplemented with periodic
or one—time measurements of specific studies. Data from permanent
stations which have historically existed in the Harbor and
nearby waters of the Strait are generally contained in EPA’s
Water Quality Data Storage and Retrieval System (STORET) (1978).
The main STORET stations operating during the past 14 years are
shown in Figures IV-l and IV-2.
1. STORET
The majority of STORET stations are the result of long-term
studies of one or more years duration by the University of Wash-
ington (UW) and the EPA. The U.S. Public Health Service, with
the assistance of the University of Washington carried out moni-
torin during the 1962 — 1964 period at a minimum of 70 stations;
nowever, due to the close proximity of some of these stations,
the researchers designated 18 standard station locations for
data analysis (Sartsch et al. 1967, USD1 1967). Refer to Section
IV.B.5 for a summary of this data.
The EPA conducted three separate water quality surveys during
the period 1970 - 1972, monitoring 25 stations. Data from each
survey is summarized in its respective report (USD1 1970, EPA
1972a, 1972b). A discussion and analysis of the data appears in
Section IV.B.5. In addition to these two intensive water
quality study periods, other data exists at only a few stations.
Washington DOE implemented six long-term monitoring stations in
1967. By 1969, monitoring was begun on three additional stations.
Six of thesenjne stations were abandoned in 1970. Of the three
174

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- -- 12010 ’
I 1120—USGS I
I 1543—EPA I
I IJDF—DOE I
I STRAIT OF JUAN DE FUCA
I
L4 8’lO’ 12048528
I 1208520
EdIz 543142•
- Pbrl 4ng.I.s Harbor 543141
i i 3139 543140
.543136
1
123 o ;
123’
48 1o’
I Prot.cflon
1’ b
I—
t
I
Figure IV-l. MAIN STORET WATER SAMPLING STATIONS, PORT ANGELES AREA, WASH
Source: Storet, retrieval of December 12, 1978

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12t’2a 12 ’27
1232 6 12f25 12S’24 i2 f 23
Strait of Juan de Fuca
4V09’ JDFOO4
.
543136
Figure IV-2. MAIN STORET WATER SAMPLING STATIONS, PORT ANGELES HARBOR, WASH.
Source: Storet, retrieval of December 12, 1978
123 22
1221 12S’20
0 1
I — —
mli.s
480%1
KEY:
543 — EPA
PAH — DOE
JDF —DOE

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remaining, one (PAHOO6, located north of the ITT Rayonier mill)
was closed down in 1975; and the other two (PAHOO3, located east
of the Crown Zellerbach mill, and JDFOO5, located in Sequim Bay)
are still maintained (Figure IV—2).
The STORET system is set up to accomodate data on nutrients as
well as standard oceanographic parameters. STORET data in the
Port Angeles area, however, consists mostly of temperature,
salinity, dissolved oxygen (DO), and a Pearl—Benson Index (P31)
test for spent sulfite liquor (SSL) (see Pearl and Benson
1940 and Barnes et al. 1963). In addition, all readings are
identified as to date, time, and depth. In general, readings
tend to be periodic (often monthly), but in some cases, the U.S.
Public Health Service studies recorded on an hourly basis during
daylight hours.
2. Crown Zellerbach
Very few studies of water quality in the vicinity of Crown Zeller-
bach’s effluent discharaes have been conducted. Some of the early
water quality studies in the Harbor pertain to Crown Ze.L.Lerbacii
discharges. The studies on sludge beds in the early 1960’s
are particularly relevant. However, in 1964 and 1967, Crown
Zellerbach made major changes in its waste discharge points,
routing some waste streams to the Strait in 1967. In 1971, these
discharges were combined into a submarine diffuser system. The
early water quality studies in the Harbor are discussed as
studies by ITT Rayonier and government agencies below in this
section. The sludge beds are discussed in Chapter VI.
Crown Zellerbach conducted some limited studies of zinc levels
near its diffuser outfall in 1972 (Aspitarte and Smale 1972).
Samples taken from the Crown Zellerbach clarifier showed zinc
levels of 12,000—16,000 jig!], with turbidities of 27—39 Jackson
Turbidity Units (JTU). At dilutions of 1:100 with water,
177

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burbidity levels were measured in the laboratory to be 0.15 -0.17
JTtJ. In situ water quality samples taken at the boundaries of
the diffuser dilution zone showed turbidities of 1.0—4.0 JTU,
indicating dilutions of roughly 1:10 - 1:60. Corresponding
zinc levels ranged from 25 pg/i up to 163 ug/l, the upper limit
being in excess of the 100 pg/i state standards. Those conditions
did occur at only a few stations and during slack time periods.
DOE conducted a follow-up study with two grab samples (Pine 1972)
and found zinc levels to be within the standards. DO and pH were
also noted to be within Class AA standards.
A brief suznmaryof general water quality in the vicinity of the
outfall was carried out in 1978 by Crown Zellerbach personnel
(Young and Cormack 1976). Sampling was carried Out on June 1.5,
1976, during a 2½ hour period. 1ater was sampled for temperature,
DO, p , and total zinc. Temperatures ranged from 45 — 48°F (7 —
9°C). DO was less than the Class AA standard of 7 mg/i at all
measurement times and stations, with surface measurements ranging
from 6.5-6.8 mg/i. The report hypothesized upwelling as an
explanation of this oxygen depletion. pH was nearly constant
within the range 7.8—7.9. Total zinc levels were 0.05—0.09
mg/i measured halfway to the bottom. This is within Class AA
standards.
Except for bioassays, no other water quality studies have been
conducted near the Crown Zellerbach discharge point. No further
studies are known to be planned by agency personnel at this time.
3. Fibreboard
No water quality studies were carried out by Fibreboard, Inc.
4. ITT Rayonier
The ITT Rayonier mill has conducted numerous studies over the
past two decades, often in response to agency studies or to
emphasize the industry’s viewpoint that certain permit require—
ments were not justified. Many of the studies were never
178

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formally published and exist as raw data accompanied by notes
and maps. Others, published by the mill as reports or included
in internal or external correspondence, are discussed below,
covering the period from 1958-1977. More recent reports by
ITT Rayonier have not yet been published.
Charnell (1958) reported on a series of water quality studies
conducted by ITT Rayonier along 5 transects (23 stations) span—
fling the Harbor and waters within 1 to 2 miles east and north-
east of the mill. Samples were collected from each
station at the 3 ft depth (.9 m), 15 ft depth (4.5 m), and
3 ft from the bottom (.9 m). In addition to discussing brief
observations of the currents and biological conditions along
the transects, SSL and DO were measured monthly from October
1956 to March 1958. SSL levels (3 ft depth (.9 in)) were
generally below 1000 mg/i SSL (which the Washington Department
of Fisrkeries CWDF) then considered to be the tolerance limit
for salmon) (Williams et al. 1953). However, near the mill,
maximum SSL values (3 ft depth (.9 in)) of over 5000 mg/i
were recorded. Dissolved oxygen concentration ranged from
below 2 to 8 mg/i measured at a 3 ft depth (.9 m). It
is interesting to note that the near-surface profile roughly
approximates simultaneous profiles taken at the 33 fathom depth
(200 ft) in the Strait. Thus, near—surface waters near the
mill approximate the anoxic conditions found in deep offshore
waters. Such waters are typically used by scavenger organisms
at a low level of ecological productivity. One of the major
findings by Charnell was that low levels of DO coincided closely
with areas of higher SSL concentrations.
In the early 1960’s, ITT Rayonier undertook a series of short
studies, which were then combined as a long term monitoring
program. The first studies were carried out in 1961 and 1962
(Stein, Denison and Isaac 1962, 1963) and a second group was
carried out mainly in 1964 and 1965 (Stein and Denison 1966).
The studies report hydrographic and biological information as
well as water quality. The major water quality parameters
measured were SSL, DO, temperature, pH and salinity. In general,
DO concentrations ranged between 4 and 5 mg/i with some readings
lower than 4.0 near the mill and at depths over 50 ft U4..7 in).,
179

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pH values were reported to range from 6.4 to 7.4 near the mill,
with the outer Harbor being generally in excess of 7.6. The
report concluded that the installation of extensive abatement
facilities (e.g. primary treatment) would not increase or enhance
water quality in the Harbor (Stein and Denison 1966).
During 1970 and 1971, ITT Rayonier conducted hydrologic studies
in order to comply with requirements to install a submarine
deepwater outfall (Tollef son, Denison and Tokar 1971). The
data gathered did not involve water quality, but did address
current directions and dilution ratios (dye studies). From the
measured dye dilutions, the authors calculated that based on a
background DO level of 7.1 mg/l, DO at the surface boil might
be as low as 0.6 mg/l; however, this would rapidly rise with
distance from the outfall, giving DO readings of 4.0 at a dis-
tance of 50 yards (45.7 rn), 5.0—6.0 mg/l at 100 yards (91.4 in),
and 6.9 mg/l at 200 yards (182.9 m). The report also correlated
effluent dilution with pH depression as follows in Table IV-3.
The report predicted that normal effluent dilutions for the
submarine outfall would range between 1:25 and 1:75. With this
dilution ratio, the authors state that under worst case condi-
tions, Class AA water quality standards would be met.
During 1975 and 1976, ITT Rayonier installed a secondary treat-
ment pilot plant and carried out studies on effluent discharges.
These studies bear more on effluent composition and toxicity
than on receiving water quality and are discussed in Chapter V.
Fagergren (1976) performed a transect study aimed at
documenting water quality conditions in and near the
effluent plume. A small plane was used to direct the boat to
areas of maximum color, thereby locating in the plume. The study
was undertaken during the suxmner of 1976 (June through August),
at which time the author expected a high DO depression from
natural factors. DO concentrations ranged from slightly above
7 mg/l to a low of 3.7 mg/l. pa generally ranged between 7.0
and 8.0. Salinity ranged between 24 and 32 ppt, while SSL
180

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Table IV-3 CORRELATION BETWEEN ITT RAYONIER EFFLUENT DILUTION
AND pH DEPRESSION IN 1971 (Based on Tollefson,
Denison and Tokar 1971)
Dilution Resultant
Effluent:Seawater pH De pression
1:7 —1.0 unitS
1:20 —0.5 units
1:50 —0.1 units
1:100 effect unineasurable
181

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concentrations peaked at roughly 155 mg/i. In cases where high
SSL was detected, there was a strong correlation with depressions
in values of DO, salinity, and to a less obvious extent, pH
(see Figure IV—3).
High SSL concentrations (above 25 mg/i), w iich seem to correlate
with low DO levels (below 5.0), were found at several hundred
meters from the diffuser and in one case at more than 1,000 meters.
Several DO readings below 4.0 were found at distances of 100 to
300 meters from the diffuser. Corresponding pH levels were in
the range of 7.0-7.1, considerably lower than the equilibrium
value for seawater.
In May 1977, ITT Rayonier conducted field samplings designed to
analyze the effects of certain mill waste streams on receiving
water quality near the outfall (Denison and Fagergren 1977,
Fagergren and Rogers 1977). The data indicated that DO was, at
times, depressed by 0.5-1.5 mg/i in the vicinity of the
extended outfall, which the authors stated constituted a techni-
cal violation of water quality standards (Denison and Fagergren
1977)
The authors hypothesized that this resulted from certain sewer
streams which imposed an inunediate oxygen demand (IOD) due to
elevated SO 2 levels. The mill streams most likely to cause such
an effect were deemed to be the acid plant and blowpit recovery
sewers. The hypothesis was tested by first diverting these
streams, and then by bypassing them directly to the outfall.
During the diversion, DO depression decreased to 0.5, while
during bypass operation, it increased to 1.8 mg/l.
During the 1977 studies, DO levels were generally higher than
6.0 mg/i, with low readings occurring when extra “square acid”
(an acidic, untreated, highly concentrated portion of the mill
effluent stream) from the two sewer systems was added. pH
remained generally above 7.5, even when acid was added. SSL
levels ranged from 0 — 150 mg/i during most of the readings, show-
ing no clearly defined relation to DO. It appeared from the data
that DO was the parameter most significantly affected by diver-
sions and bypasses of the two wastewater streams under study.
182

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SSL ma/I
SURFACE SSL AND D.O. CORRELATIONS
(DERIVED FROM FAGERGREN 1976)
E
0
0
7.5
.
7.Cs S
.

i...
.
.
85 —
• 5..
• .•.•
, •_
•• S
0
ed.
I
.
.
S
S
:
.
I
I

S
—
. 0 •
I
•
0
25
50 75 100 125 150 175
200
225
Figure IV-3.

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5. Studies by Agencies and Others
Early studies in the Port Angeles area were conducted for the
Washington State Water Pollution Control Commission (WPCC) in
the 1950’s (Peterson and Gibbs 1957). Peterson and Gibbs moni-
tored SSL, DO, temperature and salinity for forty stations
located in the Harbor and in the Strait on the outside edge of
Ediz Hook. High SSL readings coupled with DO readings in the
range of 0.0 — 4 .0 mg/i were found near the ITT Rayonier,
Fibreboard, and Crown Zelierbach mills in the Inner Harbor, and
along the western portion of the outside edge of Ediz Hook near
Crown Zellerbach. The study concluded that the Harbor was sub-
ject to frequent sub-standard oxygen conditions. In addition,
the area had high levels of bacterial contamination, and SSL
values in excess of known fish toxicity limits. The study found
that although water movement was relative].yrapid in the Strait
adjacent to Crown Zellerbach, high SSL values did occur near
Ediz Hook, indicating that thorough dilutions and dispersion
of Crown Zellerbach effluent was not always achieved.
In conjunction with research on the Port Angeles Harbor sludge
beds, WPCC conducted analyses of DO, chlorides, SSL, and volatile
solids at 18 stations in 1961 (Ott, Livingson and Mills 1961)
These were samples taken at heights of one foot (.31 m) above
Harbor bottom with water depths at these points ranging between
10 and 50 feet (3.0 - 15.2 m); chloride concentrations between
4.0 and 8.0 ppt. SSL ranged from 7 to 1630 mg/l with good corre-
lation to DO depression in most instances (see Chapter VIII for
discussion of similar correlations).
In late 1961 the State of Washington requested assistance from
the U.S. Department of Health Education and Welfare (HEW) to
help prevent and control the pollution of Puget Sound and its
tributaries and estuaries. The state indicated that seven pulp
and paper mills which included ITT Rayonier were largely respon-
sible for the water pollution problem in these waters (HEW 1962).
As a result of the state’s request, a conference under the
terms of the Federal Water Pollution Control Act (P.L. 660) was
held in Olympia, Washington on January 16 and 17, 1962. To
184

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abate the pollution problem, the conferees recommended a joint
action program be conducted by the state and federal governments.
Part of the program included field quality conditions in the
vicinity of the seven discharging mills (Bartsch et al. 1967).
In addition to water quality, circulation studies (see Chapter III),
biological and bioassay studies (see Chapters V and VI) were
also conducted. The U.S. Public Health Service, WPCC, State
Department of Game and Fisheries, universities and industries
participated in the program (Bartsch et al. 1967). In March
1967, the results of the field investigations were issued by
the Federal Water Pollution Control Administration (FWPCA)
(USD1 1967)
The monitored water quality parameters were reported in terms
of vertical effluent (SSL) distribution, SSL surface distribution,
and patterns of DO, salinity, temperature, pH and water trans-
parency. SSL concentration was generally found to decrease with
increasing depth. In some cases the effect was quite rapid
(falling to less than 5 percent in the top 10 feet), while in
others, only minor decreases were noted (Figure IV—4). Surface
SSL concentrations ranged up to 14,450 mg/i during some periods
of the 1962 — 1964 monitoring program.
The average surface SSL obtained from November 1962 through
December 1973 shows the highest concentrations near the ITT Rayon-
ier mill (Bartsch et al. 1967) (Figure IV-5). During the study,
ITT Rayonier shut down operations during an 11 day period (approx-
imately August 19—30, 1963). Comparing the surface SSL with
that obtained subsequent to the mill’s start-up shows a decrease
in surface SSL during the ITT Rayonier closure (Bartsch et al.
1967) (Figures IV—6 and IV—7). Data presented from a typical
period on December 10, 1963, show surface SSL concentrations of
up to 750 mg/i in the same location as the 5.0 mg/i DO level,
while in portions of the Harbor, less than 10 mg/i SSL corres-
pond to DO levels of 7.0. pH does not seem strongly coupled
geographically to SSL, but does suffer depressions of 0.50 units
near the mill outfalls and sludge beds.
185

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$ S L (ppm)
$ L (ppm)
100 150 200 0 200 400 600 800 1000
0
Figure IV-4. VERTICAL DISTRIBUTION OF AVERAGE, MAXIMUM, AND
MINIMUM SSL CONCENTRATIONS AT FOUR STATIONS IN
PORT ANGELES HARBOR; DATA FROM OCEANOGRAPHIC
STUDIES, SEPTEMBER 1962 TO JANUARY 1964
Source: U.S. Dept. of Interior 1967
I0
z
I
I-
a,
I II
0
30
I-
Lu
z
I .-
a,
Lu
a
. - l
MIN. AVERAIC Max.
0 50
0
iii
Lu
z
20
a.
Lu
a
3C
I I 1
-I!__
.1/
:‘/
Mar/mum ‘35X
I- —4
186

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12f29 121’28 - - I2 f27
12:28 12f25 12S24 12f23
Figure IV-5. AVERAGE
SURFACE
SSL
IN PORT
ANGELES HARBOR, WASHINGTON
NOVEMBER
1962 -
DECEMBER 1963
Source:
Bartach
et
al.
1967
Strait of Juan do Fuca
12322 12121 12S’20
01
muss
4 8’oIJ
0 d
)

-------
Strait of Juan de Fuca
L Figure IV-6. AVERAGE
SURFACE SSL IN PORT ANGELES HARBOR WASHINGTON
AUGUST
30,
1963
48’OS’
‘-a
Harbor
)
Source: Bartsch a!. 1967

-------
Strait of Juan de Fuca
C Figure IV-7. SURFACE SSL
SEPTEMBER 8,
IN PORT ANGELES HARBOR, WASHINGTON
1963
Source: Bartsch et al, 1967

-------
Three water quality surveys were carried out at Port Angeles by
government agencies in the period 1970 — 1972 (USD1 1970; EPA
1972a 1 1972b). These studies were designed to follow up Washing-
ton State Surveillance data taken during the period September
1969 — April 1970, and to generate some baseline data to provide
before and after comparisons of primary treatment and effects
of the• ITT Rayonier submarine outfall.
Survey #1 was carried out on July 23, 1970 (USD1 1970). Sampling
was conducted for total coliforms, SSL, pH, DO and salinity at
depths ranging to 70 feet (21.3 m). A comparison of surface SSL
concentrations on this date ranged from 1 — 204 mg/i with surface
DO ranging from 5.8 to 6.8 mg/i, showing roughly an inverse cor-
relation (Figure IV—8). pH variation was only 0.3 units with no
strongly discernable pattern. Total coliforni organisms were
generally 20 or less per 100 ml except at a point immediately
east of the ITT Rayonier mill (60 Most Probable Number (MPN)),
and at several points near the Fibreboard plant (30, 100, 2300
MPN, respectively).
Survey #2 was carried out in May 1972, several months prior to
installation of primary treatment and the deepwater diffuser
(EPA 1972a). Sampling was completed on May 3 arid 4, 1972 by
EPA and supplemented by DOE data from other dates during May
(DOE 1972) which were oriented toward aquatic toxicity (see Chap-
ter V). SSL levels at most stations were considerably higher
than in the 1970 survey. Surface SSL ranged from 9 to 2000 mg/i
in the Harbor. SSL readings of 100 mg/i and 96 mg/i were taken
offshore of Morse Creek and Green Point, respectively, with
levels of 9 and 5 mg/i at the base and tip of Dungeness Spit
(Figure IV—9). DO values ranged from 6.9 to 9.3 mg/i during the
two day sampling, with the lowest DO 7alues correlating to high
apparent SSL concentrations. The highest SSL readings in this
period occurred from the central Harbor, north toward Ediz Hook,
rather than near the mill outfalls. SSL levels of 1300 and 610
mg/i were recorded near ITT Rayonier. The pH showed a depression
of 1.1 units from the background levels of 7.8. Bacterial coliform
levels were generally 30 or less and do not correlate with SSL
levels in any obvious manner.
190

-------
en
0
a
SSL mg/I
SURFACE SSL AND D.O. CORRELATIONS, PORT ANGELES HARBOR,SURV Y #1
Source: USD1 1970
a
a
,& -
6.S
8.C • us
6. ? ‘ •. S
Sc.
—
.
u .4
s.a
.
5
I.
6.1
S
pJL •
5.
LI
S
I-
.
5.7
5.6
s.e
5
0
23
50
75
100
125 150 175 200 225
Figure IV-B.

-------
9
SSL mg/I
Figure IV-9. SURFACE SSL AND D.O. CORRELATIONS, PORT ANGELES HARBOR, SURVEY 1 2
Source: EPA 1972a

-------
Following installation of primary treatment and the submarine out-
fall at ITT Rayonier, Survey #3 was conducted by EPA on October 31
and November 1, 1972 (EPA 1972b). The study was never written
up or published but the raw data is available and follows the
format and station locations of Survey #2 (Figure IV—lO).
Survey #3 measured SSL levels to be significantly lower than
Survey #2 and somewhat lower than Survey #1 (EPA l972b). SSL
levels ranged from less than 1 to 146 mg/i with many readings
ranging between 10 and 40 mg/i. Surface DO was generally be-
tween 5.8 and 6.5 mg/i, with two readings below 5 mg/i between
Lees Creek and Morse Creek (DO = 4.2 mg/i, SSL = 146 mg/i). pH
ranged between 7.4 and 7.7 with no demonstrably strong correla-
tions to other parameters. Coliform counts range between 0 and
2100, but seem to correlate more closely to the Port Angeles
municipal discharge location than with the ITT Rayonier outfall
or with SSL levels.
In late 1974, the U.S. EPA office in Denver published an evalua-
tion of ITT Rayonier’s extended outfall (EPA 1974). Water
samples were collected and analyzed to provide field calibration
for aerial photographs of circulation studies. Samples were
taken at eleven stations in the Harbor and near the outfall,
with one station in the Strait north of the tip of Ediz Hook.
Data was collected on April 23, 1973. Except for the one
sampling station immediately west of the mill, the DO and pH
readings were all above 9.0 and 7.5 mg/i, respectively.
The total suspended solids (TSS) for these same stations were
below 23 mg/i. The one station west of the mill had an SSL reading
of 233,000 mg/i, a TSS reading of 31 mg/l, a pH of 2.5, and no
measurable DO. Since readings near the extended outfall were
nowhere near these values (SSL2O mg/i, TSS19 mg/i, D09.4
mg/i, pH=7.5), it is not clear whether the effect might be due
to sludge beds, unusual current conditions or a shoreline dis-
charge from the mill. The data seem too consistant across the
various parameters for the readings to be completely erroneous.
193

-------
I
I
75 100 125
150 175 200
SSL mg/I
SURFACE SSL AND D.O. CORRELATIONS, PORT ANGELES HARBOR, SURVEY #3
Source: EPA 1972b
00
S.
• S.
•
• III S
IS IS
I
•5 5
I
I
I
2
5A:
—
I
S.C
,
4
-c
S
25 50
225
Figure IV-1O.

-------
The most recent water quality surveys performed by regulatory
agencies were those conducted by DOE during May 22—27, 1975
(Moore 1976). The water quality data gathered included SSL, pH,
salinity, suif ides, DO, and was coupled with livebox bioassay
tests. This study was designed to test water quality improve-
mentsin the eleven years between 1964—1975, based on compari-
Sons with 1964 bioassays conducted by the WPCC (Ziebell et al.
1964). Unfortunately, the 1975 studies were taken during a
period when the ITT Rayonier mill, had been on strike and shutdown
for more than a month. The water quality is therefore presumably
indicative of chronic effects such as sludge beds, but not of
mill discharges. The study sampled locations near the ITT Rayon-
ier, Fibreboard, and Crown Zellerbach sludge beds and found
oxygen and sulfide conditions much improved, with DO levels above
6.5 mg/i and sulfide levels less than 3.0 mg/i. pH levels were
generally 7.3.
C. EPA FIELD STUDIES
In June 1979, the U.S. Environmental Protection Agency (with
assistance by NEC and EHI staff) undertook a short—term synthetic
field program to attempt documentation of currents, water quality,
and toxicity in the vicinity of Port Angeles Harbor immediately
before the installation of secondary treatment processes by
ITT Rayonier. Results of current studies are mainly covered
in Chapters III and VIII, while toxicity is covered in Chapter V.
Here we discuss water quality parameters and applicable dilution
information.
1. Sampling Methods
Water quality measurements were made at Port Angeles Harbor and
points east during June 7 - 8, 1979 as shown in Figures IV-l1
IV-12. Concurrent measurements of In—plant effluent were also
made at the ITT Rayonier pulpmill, throughout the sampling
195

-------
hundreds of feet
Outfall
67
C.
.12
Strait of
Juan De Fuca
EdIz Hook
Crown Z&l.rbach
Port Angeles Harbor
10.
ITT Rayonler
Figure IV-11. WATER QUALITY STATIONS OF THE R/V THUNDER-
BIRD IN THE VICINITY OF PORT ANGELES
HkRBOR, JUNE 7 & 8, 1979.
r’
196

-------
hundreds of feet
Outfall
+ ‘21
17 19
at... •20
‘U j5
Figure 117 -12.
WATER QUALITY STATIONS OP THE R/V STREETER
IN THE VICINITY OF PORT ANGELES
HARBOR, JUNE 6 & 7, 1979.
Strait of
Juan De Fuca
EdIz Hook
Crown Zeflerbach
Port Angeles Harbor
18.
ITT Rayonler
197

-------
period. These measurements were used for calibration purposes
and for dilution calculations. Monitoring was conducted
from the craft R/V Streeter on June 6 — 7, 1979 and by the craft
R/V Thunderbird on June 7 - 8, 1979. Positions of both vessels
were fixed by a light aircraft using a mini-ranger system.
Mini—rangers were emplaced at four positions in the area. Data
not taken directly from field measurements were derived from
sample analysis by the U.S. Environmental Protection Agency
laboratories at Manchester, Washington and Corvallis, Oregon.
In—plant sampling was conducted from the entry point of the
submarine diffuser (Pipe #001) inside the mill, with the excep-
tion of one sample taken from the blowpit (June 5, 1979).
Thus, all samples represent primary treated effluent, except
the June 5 blowpit sample. In-plant samples were analyzed for
P31, biological oxygen demand (BOD), dissolved organic carbon
(DOC), total organic carbon (TOC), ammonia and nitrate nitrogen
dissolved ortho-phosphate, total phosphorus, suspended solids
(SS), chemical oxygen demand (COD), total volatile solids (TVS),
and total solids (TS). The data from these tests appear in
Table IV—4.
Data was collected at 4 stations (designated 18, 19, 21, 22)
in Port Angeles waters by the R/V Streeter on June 6 and 7,
1979. All samples were taken at surface depth (0.5 meters),
except fluoroinetric samples. Surface samples were analyzed for
P31, DOC, TOC, nitrate nitrogen, ortho-phosphate, total phosphor-
us, and SS (Table IV—5). The majority of these data were taken
on June 7. Fluorometric measurements were made at several depths
for later comparison against laboratory calibrations of In-plant
effluent dilutions (Table IV-6). These data were taken for
the purposes of determining normal plume dilution and vertical
location.
The craft Thunderbird collected water quality and bioassay samples
on June 7 and 8, 1979, from 12 (total) stations along the plume
198

-------
Table iv-4. WATER QUALITY DATA COLLECTED FROM ITT RAYONIER PLANT EFFLUENT,
JUNE 4, 5, 6, 7, 8, 1979
foul
DI..olvsd
Total
Vol.
I
Total
Dat. a U&uple
organiu
ortho
Su.p.ndsd
Solid.
•
Solid. COD
Vol. Total
Tlao
1919
Ds.crip—
tion’
0003
911 la p/ i)
0003
(.9/1)
000 000jj
(mg/U (.9/1)
2O
(m g /I l
POC
(.9/1)
Carbon
(mg/I)
P0
(.9/1)
(.9/1)
(mg/ i)
( .9/1)
(.9/1)
Solid. Solid.
Jun. 4
0900
fInal
BUlu.nt
1020
loss
1158
•
0.40
1022
•
42.0
4.6000
420
503.0
N/b
573.0
18.0
490.0
3w ,. 3
0.50
0953
final
93.0
3,600.0
395
463.0
M/D
535.0
40.0
520.0
If I luant
M/D
Slow pit
1.160.000.0
(mill)
1000
final
Uflu.nt
Jwi. 6
0035
final
25.0
920.0
960.0
0.34
Bf(lu.nt
0900
•
48.0
1000.0
1020.0
0.40
1000
1001
•
•
30.0
780.0
820.0
1100
•
118.0
2500.0
2900.0
1.1
1200
•
21.0
680.0
690.0
1030
•
7,400.0
3065.0
903.0
930.0
970.0
Jun. 7
1703.0
1038.0 1570.0
0745
ftn.1
20.0
7,500.0
600.0
620.0
0.30
0.34
10.0
If I lu.nt
0750
31.0
38.0
3590.0
1288.0 2423.0
0900
•
37.0
8,200.0
890.0
940.0
0.23
30.0
40.0
3000.0
1563.0 2907.0
1000
28.0
9,200.0
1000.0
1010.0
0.35
1003
10.0
2301.0
1319.0 2515.0
1100
29.0
1,600.0
844.0
000.0
840.0
0.78
0.80
32.0
43.0
1633.0 3162.0
1200
•
28.0
5,400.0
1180.0
1230.0
0.58
1015
775.0
800.0
1045.0
835.0
Jun. 0
16.0
29.0
1056.0
0020
final
25.0
7,400.0
584.0
640.0
600.0
0.35
0.40
IItlusnt
S
All .up i. . vsr• taksn Ito. pip. 001 .i ..qiwnt to prinary tx.atnant amcspt Blow PIt ..apl..
. 5
Pioas..y lakan .lowltsn.ou.ly.

-------
Table IV-5. WATER QUALITY DATA COLLECTED BY THE R/V STREETER IN THE VICINITY
OF PORT ANGELES HARBOR ON JUNE 6 and 7, 1979
l I .tsr.
I. i9ht
Total
Dissolved
(ye ))
Ur
go
D lUus.r
Station Center
Dat. $
Ti..
1979
Dsptb
I .)
8e11nLt
/ ..
Water
Ts .
C
Tran.-
aitt—
and
PSI
(.9/1)
DCC
(. /1)
019.
Carbon
(mu/ I)
111103
4 1102
(.9/1)
Ortho
P0.
(.9/1)
Total
Phosphate
(. /l)
Suspended
Solid.
(ui9/l)
Susp.nd.d
Solid.
(.5/1)
31.3 10.3 97.5
31.3 10.3 99.0
31.3 10.2 99.0
31.3 10.3 99.0
31.2 10.3 98.5
31.2 10.2 98.5
‘ S. )
0
0
June 6
14 846 0743 0
14 846 0743 4
14 846 0743 8
15 650 0851 0
is 650 0851 4
is 6S0 0851 8
18 731.5 0935 0.5 (3)
19 457.2 0944 0.5 (3)
19 457.2 0950 0.5 (3)
19 457.2 0954 0.5
9 437.2 0954 0.3
19 457.3 1001 0.5
19 457.2 1005 0.5
19 4S7.2 1003 0.5
19 497.2 1005 0.5
19 453.2 1014 WD
19 457.3 1014 0.5
19 457.2 1011 0.5
Jun. 7
21 801.9 0743 0. 5
21 801.9 0743 0.5
21 801.9 0742 0.5
21 801.9 0750 11/0
31 801.9 0750 11/0
21 801.9 0150 11/0
31 801.9 0759 11/0
21 801.9 0159 11/0
31 801.9 0759 11/0
21 801.9 0805 11/0
21 801.9 0805 0.5
21 801.9 0805 0.5
21 801.9 0810 0.5
21 801.9 0810 0.5
21 801.9 0810 0.5
22 1280.2 0904 0.5
22 1380.2 0901 0.9
22 1280.2 0904 0.5
22 1280.2 1231 0.5
25.0
28.0 (3)
23.0 (3)
26.0
25.0
23.0
1.0 3
1.03 1.6
2.0 1.6
44.0 4.6
41.0 4.6
42.0 1.8
35.0 3.8
34.0 3.6
31.0 3.4
35.0 4.0
35.0 3.6
33.0 4.0
19.0 2.8
20.0 2.2
26.0 2.8
5.0 2.0
7.0 1.8
6.0 3.0
1.0 K 1.2
3.0 1.2
2.0 1.2
4.0 1.4
1.6
1.6
4.8 0.18 0.02
5.4 0.17 0.02
5.2 0.17 0.03
4.0 0.18 0.01
4.4 0.18 0.02
5.0 0.18 0.02
4.0 0.17 0.02
4.8 0.17 0.02
4.0 0.17 0.02
2.8 0.31 0.02
3.2 0.20 0.02
3.2 0.20 0.02
2.0 0.20 0.01
2.0 0.20 0.04
2.0 0.20 0.04
1.2 0.22 0.05
1.2 0.22 0.05
1.2 0.22 0.05
2.4 0.20 0.08
0.060
0.060
0.060
N/U
0.062
0.060
0.058
0.060
0.060
0.063
0.063
0.064
1 1/0
0.066
N/b
0.056
0.056
0.055
0.068
5.0 5.0
7.0 7.0
4.0 4.0
5.0 9.0
4.0 5.0
6.0 7.0
4.0 5.0
3.0 4.0
4.0 4.0
3.0 5.0
1.0 1.0
3.0 6.0
5.0 6.0
4.0 5.0
4.0 6.0
3.0 5.0
3.0 4.0
6.0 7.0
7.0 15.0

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Table IV-6.
CONCENTRATION OF PULPMILL WASTE
R/V STREETER, JUNE 7, 1979
BASED ON IN SITU FLUOROMETRIC MEASUREMENTS:
Location Time Period Depth (m) Concentration Range
Station B 48° 8.6’ N
123° 23.2’ W
0.5
2.0
4.0
6.0
8.0
10.0
12.0
14.0
15.0
0.5
2.0
4.0
6.0
8.0
10.0
12.0
14.0
15.0
0.5
1.0
2.0
3.0
4.0
5.0
6.0
.004 2
.004 2
.0034
.0034
.0026
.001
.0004
.0004
.0004
.001
.001
.001
.001
.001
.001
.001
— .0157
— .0157
— .0126
— .0126
— .0094
— .003
— .0012
— .0012
— .0012
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
— .003
— .003
— .003
— .003
— .003
— .003
— .003
Station
A
48°
8.5’
N
0828
—
0839
123°
22.4’
W
0851
—
0900
Station
C
Of f
Green
Point
1210
—
1216

-------
and two control stations. These data appear in Table Iv—7
and include all parameters monitored by the R/V Streeter plus
BOD.
2. Mill Data
Data taken within the mill during June 4—8, 1979 included P31,
ammonia nitrogen, BOD, DOC, TOC, phosphorus, SS, TVS and PS.
Ammonia nitrogen varied greatly over the period (almost by a
factor of 4), from 27.0 to 93.0 mg/i. P31 varied only by a
factor of 2, ranging from 4600 to 9200. BOD also varied by
roughly a factor of 2. All other parameters measured, except
TVS, varied by factors of 2 to 3 over the five day period. TVS
was the most stable factor, witli a variation of only 1.5. Values
of the various parameters were comparatively high on June 7 - 8,
when receiving water sampling was performed.
3. Dilution Calibrations
Fluorometric data was calibrated against dilutions of mill ef flu-
ent to derive actual dilutions of effluent in the receiving
waters. These dilutions have been discussed in Chapter III and
are only sununarized here in the context of water quality impli-
cations. Near the leading edge, where the plume first surfaced,
tne highest concentrations ranged from 1:60 to 1:225 and occurred
at depths of 6 - 10 meters. Near the diffuser, the plume center,
dilutions of 1:125 to 1:450 occurred on the surface. Of f Green—
point, values ranged from 1:330 to 1:1000; however, data from
other stations indicate that the initial dilution is much more
rapid than dilutions subsequent to when the plume surfaces.
Effluent often travels considerable distances with little addi-
tional dilution (see Table IV—7).
Based on the calculated dilutions, maximum potential water qual-
ity changes due to effluent effects are summarized in Table IV-8.
202

-------
Table IV- ?. WATER QUALITY DATh COLLECTED BY THE R/V THUNDERBIRD IN THE VICINITY
OF PORT ANGELES HARBOR, JUNE 7 and 8, 1979
C
0

2
“
etsre
from
DIffuser
Center
—
3
Date 6
Time
1979
Sal in-
Sty
/.
0.0.
lag/ i)
02
S
Satin-
etlon
Water
Teas.
C
Conduc-
t lvity
681
(rn/I)
2
o in
.4 .4
0
g
(mg / i)
Di .—
(‘ol)
NT
Total
oIved
Total
Stic-
Stis-
EEC
orn .
cerls,n
C li i i
I1 ( S
2
c’rtho
4
‘hoe-
phate
rnd d
co lldq
pind.-d
Sal id
(eq/I)
(imi/I)
lcm,/1)
(imp/I)
faq/I)
(rn/I)
fm/I)
(rn/I)
2.5
5.9
3.0
2.3
3.5
2.1
2.5
5.6
3.0
2.5
3-7
2.2
2.1
6.5
3.)
2.5
4. ’
2.2
Jima 7
114
11/0
0639
0
27.97
10.55
*12.24
10.5
43000
1.1
1 14
0703
5
27.97
10.23
*09.00
10.5
43000
3.0
114
0720
30
24.66
9.34
88.32
10.0
44000
7.0
1
711.5
0816
0
27.97
10.22
108.90
10.5
43000
59.0
1
0807
5
27.97
9.72
)03.57
10.5
41000
14.11
1
•
one
so
27.97
9.56
101.86
10.5
IJOtiO
6.0
3
*180 7
0904
0
27.97
10.22
*08.90
10.5
41000
9.0
I
“
0859
5
27.97
9.55
101.76
10.5
43000
5.0
3
“
0039
10
28.32
9.53
*01.85
10.5
43500
2.0
4
2743.2
0940
0
27.97
9.09
105.27
10.5
43000
7.0
4
“
0941
5
27.97
9.54
101.65
10_S
43000
6.0
4
-
0917
10
28.32
9.36
100.03
*0.5
43500
5.0
S
4572.0
102*
0
27.97
10.38
110.60
I0.5
43000
14.0
S
1012
5
27.97
9.88
105.27
10.5
43000
13.0
5
1002
10
26.32
9.52
101.74
10.5
43500
12.0
6
2645.9
1110
0
37 .97
10.37
130.50
30.5
43000
2.0
6
•
1100
5
27.97
10.04
106.99
10.5
43000
1.0
6
1046
10
27.97
9.53
100.32
10.0
43000
1.0
7
1828.8
1140
5
27.97
9.87
105.17
10.5
43000
1.0
7
1123
10
20.32
9.34
99.52
10.5
43500
2.0
6
4389.1
1220
0
27.97
11.21
120.36
11.0
43000
3.0
Jima 8
SN
1820.6
0646
0
27.97
10.52
112.09
10.5
43000
1.1
SN
“
0642
5
27.97
10.52
112.09
10.5
43000
1.1
SN
“
0633
10
27.97
10.46
115.72
10.5
4)000
1.1
9
N/b
0610
0
28.32
10.83
115.92
10.7
43500
2 0
9
0605
5
26.66
10.72
114.91
10.7
44000
1.1
9
0600
10
28.32
10.66
113.40
10.5
43500
1.1
10
320
0721
0
29.32
10.33
110.40
10.5
43500
4.0
so
0714
5
28.32
9.99
106.76
10.5
43500
4.0
10
•
0705
10
27.97
10.18
108.47
10.5
43000
9.0
11
N/b
0831
0
26.45
10.32
110.13
10.6
43700
66.0
1 1
0828
5
28.66
10.30
109.91
10.5
44000
3.0
11
•
0920
20
29.66
9.47
101.21
10.5
44000
1.1
*2
1737.4
0915
0
28.66
9.79
104.78
10.3
44000
18.0
12
0900
5
28.32
10.32
110.29
10.5
43500
4.0
12
—
0859
10
29.66
9.63
*02.76
*0.5
44000
5.0
*3
1554.5
0917
0
28.66
11.06
119.10
11.0
44000
10.0
13
0934
5
20.66
10.6)
113.44
10.6
44000
1.0
13
0930
10
20.66
10.29
109.01
10.5
44000
1.0
1.8
1_I
2.4
5.6
2.9
1 . 8
2.0
1.1
16
2.2
1.9
1.4
3.2
2.5
2.0
1.8
12
0.6
1.6
10
1.3
1.2
1.7
0.2
2.0
2.0
.22
.04
.082
3
5
2.4
3.2
23
.00
.066
6
38
2.4
2.4
26
08
.084
4
10
5.2
5.6
.23
.10
.11
5
7
2.4
2.8
. 74
.06
080
4
6
3.2
4.0
.25
.30
.33
24
32
2.4
2 4
21
.0
N/b
2
3
2.0
2.0
.24
.07
.78
1
3
2.4
2.8
.24
.07
.078
3
5
2.4
2.4
.24
.06
.080
3
6
7.4
2.4
.24
.07
N/b
2
6
1.6
2.0
.24
07
080
S
8
2.4
2.8
.77
06
080
1
9
2.4
2.4
.22
06
078
3
8
20
2.4
77
00
.080
4
6
1.4
1.6
21
.06
078
3
4
1.6
1.6
.24
.08
082
4
6
1.6
1.6
.26
.08
.082
2
5
1.6
1.6
.22
.08
.002
4
6
1.2
1.2
.25
.00
.087
5
7
1.6
1.6
.18
06
.074
5
7
0.0
1.2
2506
.22
.07
.072
6
6
0.8
0.0
.21
.07
074
5
5
0.8
0.8
.21
07
.074
4
S
12
1.2
. 1
.06
.074
3
4
1.2
1.6
.19
06
.074
8
0
1.2
1.7
.19
06
.070
8
0
1.2
1.4
2508
.19
.06
.070
8
11
1.2
1.2
.21
.06
.076
5
6
2.2
2.2
.24
.07
.076
5
5
5.6
5.6
2506
.22
.05
.076
3
6
1.2
1.2
22
.06
074
4
9
1.2
1.2
.26
.07
.070
3
4
1.6
1.6
.16
.02
.072
5
6
1.2
1.2
.20
.04
.068
5
6
1.2
1.2
.24
.06
.074
4
5
1.6
1.6
.17
.06
.070
1
5
0.6
0.8
.21
.04
072
5
6
0.8
0.0
.2)
.05
074
4
6

-------
Table IV-8. EXPECTED WATER QUALITY CHANGES BASED ON FLUOROMETRIC
MEASUREMENTS AND IN-PLANT VALUES
Parainete r
Minimum
final
ef .luent
value
In near plume field
below surface
1:60 — 1:225
PBI
BOD
In plume — where
plume surfaces
1:125 — 1:450
Of f Green Point
1:330 — 1:1000
7400
584
600
620
0.23
0.32
18.0
1703
DOC
TOC
Ortho P04
Total P C 4
ss
COD
33 — 123
2.6 — 9.7
2.7 — 10.0
2.8 — 10.3
0.001 — 0.004
0.001 — 0.005
0.08 - 0.3
7.6 — 28.4
16 — 60
1.3 — 4.7
1.3 — 4.8
1.4 — 5.0
0.0005 — 0.002
0.0007 — 0.003
0.004 — 0.15
3.8 — 13.6
7.5 — 22.5
0.6 — 1.8
0.6 — 1.8
0.6 — 1.9
0.0002 — 0.0006
0.0003 — 0.001
0.02 - 0.06
1.7 — 5.2
204

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These data were obtained by multiplying final effluent concentra-
tions by the dilution values.
It should be noted that wind conditions and turbulence were
unusually high during the sampling period. Dilutions in the sur-
face ten meters were probably considerably higher than under
more normal conditions.
Comparing the expected parameter variations in columns 2 and 3
of Table IV-8, one can immediately deduce that the measurement
methods for certain parameters were not sensitive enough, under
the weather conditions, to show variation due to pulpmill
effluents. Phosphates (and presumably nitrates, although these
were not calculated), chemical oxygen demand, and suspended
solids all showed lower sensitivities than would be necessary
to discern any patterns. Additionally, suspended solids seem
to undergo large natural fluctuations. This leaves only the
parameters P31, BOD, DOC, and TOC potentially showing patterns
correlating to effluent under normal dispersal conditions.
These will be discussed in some detail below, along with oceano-
graphic parameters.
4. Data Results
Temperature and Salinity: Water temperature fluctuated only
one degree (from 10.0 to 11.0 C) from the surface to 30 meters
depth. At most locations, the top 10 meters varied only 0.2 C
(from 10.5 to 10.7). There were no discernable effluent effects.
Salinities were not measured directly due to malfunctioning of
equipment. Instead, salinities were computed from conductivity
readings, the scale of which was too gross to register changes
due to the present or absence of effluent.
205

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Dissolved Oxygen: Oxygen levels were high and the water was
actually supersaturated with oxygen in most cases. This was
largely due to high turbulence and waves which had been oxygen-
ating the surface waters for over 2 days. The only non—
saturated reading was the one taken at 30 meters depth, and
even that reading was fairly high.
Pearl-Benson Index: Sulfite waste liquor, as indicated by the
PSI test, was generally in the expected range predicted by
dilution ratios. Stations 1 and 11 showed readings of 59 and
66 at the surface, indicating effluent present in the predicted
amounts. This was confirmed by a mini-ranger fix at Station 1.
Unfortunately, no fix was taken for Station 11.
Only these two readings are far enough above background levels
(generally 0 — 20 PBI) to definitely show patchiness of the
effluent and the turbulence of the water during the sampling
makes interpretation of the other PBI data difficult. While
there may have been effluent concentrations near other stations,
the PSI values do not clearly show this.
Biological Oxygen Demand: BOD was tested for 5, 10, 15 and 20
day incubation times. At Stations 1 and 11, where PBI values
were high, BOD was consistantly higher than other areas. Sur-
face values ranged 3.7 to 8.3 mg/i higher than typical levels for
5 day SOD, and 3.6 mg/i higher for 20 day BOD. Although these
raised BOD levels did not cause violation of dissolved oxygen
standards during the period in question, effects may be observa-
ble during calmer weather periods.
Organic Carbon: Dissolved and total organic carbon levels both
varied between 0.8 and 5.6 mg/l. The majority of values for
DOC lie between 0.8 and 2.0 which probably represent background
levels. DOC levels of 1.6—2.4 mg/i generally correspond with
206

-------
stations of PBI values between 5 and 15. Stations 1 and 11 which
had PBI values above 50 correspond to surface DCC values of 5.2
and 5.6 mg/i, respectively, a discernable jump above background
values. Interestingly enough, at Station 1 at 10 meters depth,
the PBI test shows little result, although the DOC results show
3.2 mg/i, significantly above background. This may have been a
result of effluent patchiness or may indicate that DOC can pick
up effluent fractions to which the Pearl—Benson test is insensi-
t ive.
Total organic carbon shows the same patterns as DCC, with slightly
higher levels due to the addition of settleable and suspended
organic carbon fractions. TOC levels were 5.6 mg/i at the sur-
face at Stations 1 and 11. TOC levels at 10 meter depth at
Station 1 were 4.0 mg/i. Background levels were roughly equal
to DOC values.
Nitrogen and Phosphorus: Nitrogen was measured in the mill
effluent stream as ammonia nitrogen, the main component generated
by the acidic pulping process. Upon entering the receiving
water, most of this ammonia compound either converts to nitrate
and nitrite forms or escapes as ammonia gas. Some may remain
as dissolved ammoniuxn compounds in the water, but nitrate is
usually the dominant aquatic form.
Ammonia nitrogen in the mill varied from 21.0 - 93.0 mg/l giving
a maximum expected variation in the plume of 0.75 mg/i. In
fact, total nitrate variation was less than 0.10 in all cases.
Thus much of the ammonia nitrogen must be bound into compounds
or released into the atmosphere. The fluctuations of nitrate
in the receiving water are relatively large compared to the
range in absolute values (1.6—2.6 mg/i); however, these fluc-
tuations do not seem to relate in any obvious manner to stations
in or out of the effluent. Stations 1 and 11 show levels
similar to known control stations.
207

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Phosphorus data show that the plant discharged only 0.78 mg/i
dissolved ortho-phosphate and 0.88 mg/i total phosphorus
during the study. From the dilution data, one would expect
variations in the plume due to effluent of less than 0.01 mg/i.
Since background phosphorus levels vary between 0.02 and 0.08
mg/i for ortho-phosphate, and 0.06 - 0.09 mg/i for total phos-
phorus, the effects of the effluents will generally not be
observable. At Station 1, however, levels are clearly higher,
both on the surface and at 10 m depths (indicating again
that the PBI test does not show the presence of some effluent
fractions) with ortho—phosphate levels of 0.10 and total phos-
phorus levels of 0.11. Station 11 does not show particularly
high phosphorus levels.
Solid Components: Suspended volatile solids in the mill ef flu-
ent ranged from 16-32 mg/i, while total solids discharged
ranged up to 3162.0 mg/i. This indicates that large quantities
of settleabie solids, many of which (1038 — 1622 mg/i) are
volatile (containing highly reactive and possibly toxic chemical
compounds) are discharged from the diffuser to either settle
to the bottom or be carried by bottom currents to other areas.
Unfortunately no benthic studies have been carried out in the
vicinity of the outfall and sampling of bottom water quality has
not been rigorously carried out. The one data point at consid-
erable depth in this study (30 m — Station 1) does show very
high levels of suspended solids (24 mg/i).
Volatile suspended solids in the receiving waters generally vary
from 2 - 8 mg/i with no strong correlations with P31 or other
parameters. The deep (10 m) readings at Station 1 recorded high
volatile suspended solids (24 mg/i) and total suspended solids
(32 mg/i). This may be significant since this station lies
only 731 meters southeast of the outfall and was sampled on a
flood tide.
208

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5. Conclusions
Water quality measurements during the June 6-8, 1979 period
were made under adverse weather conditions of high winds and
substantial wave action. These conditions were unfavorable
for detection of effluents of any type and generally made
sampling difficult in terms of boat drift and depth accuracy.
The high winds and rough water also tended to break up and
disperse the effluent plume which has been observed to form
near the ITT Rayonier outfall (see Chapter III and VIII.A)
Even under the adverse weather conditions, effluent traces could
be observed at several stations through high readings of PBI,
BOD and carbon. Solids showed a particularly high value at
one station in the plume at a depth of 10 meters. This, coupled
with differences in suspended and total solids measured at the
In—plant location of the discharge pipe indicate that much of
the solid material discharged by ITT Rayonier may settle to
the bottom near the diffuser or may be carried to nearby areas
by bottom currents. Light transmittance and oceanographic
data taken by the R/V Stree.ter shows no distinct effects of
the effluent on these parameters.
209

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REFERENCES
CHAPTER IV
Aspitarte, T.R. and B.C. Smale. March 12, 1972. “Sludge
Bed Survey Near Crown Zellerbach Dock Port Angeles
Inner Harbor.” Research Memorandum No. 109—9. Crown
Zellerbach Corp., Port Angeles, Washington.
Barnes, C.A., E.E. Collias, V.F.. Felicetta, 0. Goldechmid,
B,F. firutfiord, A. Livingston, J.L. McCarthy, G.L. Toombs,
N. Wal.dichuk, and R. West].ey. June 1963. “A Standardized
Pearl Benson, or Nitroso, Method Recommended for Estima-
tion of Spent Sulfite Liquor or Sulfite Waste Liquor
Concentration in Waters.” TAPPI 46(6); 347—351.
Bartsch, A.?. R.J. Callaway and R.A. Wagner. 1967. “Tech-
nical Approaches Toward Evaluating Estuarine Pollution
Problems.” IN: Estuaries (G.H. Lauff, ed.), Publica-
tion No. 83.
Charnell, H.V. June 1958. “Water Quality Port Angeles Harbor.”
5 pp. and figures.
Denison, J.G. and D.C. Fagergren. May 25, 1977. Monthly
Technical Report. Olympic Research Division, ITT Rayonier,
Inc., Port Angeles, Washington.
Fagergren, Duane C. December 20, 1976. “Water Quality Para-
meters in the Port Angeles Receiving Environment.” Olym-
pic Research Division, ITT Rayonier, Inc., Port Angeles,
Washington.
Fagergren, Duane and D.S. Rogers. June 6, 1977. “Port
Angeles Marine Water Quality: Effect of Mill Effluent
Immediate Oxygen Demand on Receiving Water Dissolved
Oxygen Depression.” Report. Olympic Research Division,
ITT Rayonier, Inc., Port Angeles, Washington.
Moore, Allen W. January 1976. “Port Angeles Harbor Field
Toxicity Tests.” IN: Port Angeles Harbor Biological
Studies, Spring 197w. Washington State Department of
Ecology, Olympia, Washington. pp. 4-29.
Ott, Charles, Alfred Livingston, and Al Mills. 1961. Water
Quality Survey: Port Angeles. FWCPA (unpublished report)
Pearl, l.A. and H.K. Benson. October 1940. “Nitrosolignin
Colorimetric Test for Sulphite Waste Liquor in Sea Water.”
PaDer Trade Journal 111(18) 235—236.
210

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Peterson, D.R. and C.V. Gibbs. 1957. “An Investigation of
Pollution in the Vicinity of Port Angeles.” Technical
Bulletin No. 23, Summer 1957. washington Pollution Con-
trol Commission, Olympia, Washington. 35 pp.
Pine, Ron. April 6, 1972. Memorandum to Jim Knudson, DOE,
Olympia, Washington.
Stein, J.E. and J.G. Denison. December 1, 1966. Port Angeles
dater Monitoring Program. ITT Rayonier, Inc., Port Angeles
Washington. 23 pp.
Stein, J.E., J.G. Denison, and G.W. Isaac. May 14, 1962.
“Port Angeles Water Quality Survey Reveals No Basis for
Recovery Requirements.” ITT Rayonier, Inc., Port Angeles,
Washi.nqtori. 41 pp.
Stein, J.E.,, J.G. Denison, and G.W. Issac. September 1963.
“An Oceanographic Survey of Port Angeles Harbor” (Pro-
ceedings of the Eleventh Pacific Northwest Industrial
Waste Conference). Circular No. 29. Engineering Exper-
iment Station, Oregon State University, Corvallis, Oregon.
p. 172—203.
Tollefson, Roger, J.G. Denison and E. Tokar. August 30, 1971.
“Outfall Location Studies - Port Angeles, Washington.”
ITT Rayonier, Inc., Port Angeles, Washington. 2]. pp.
United States Department of Health, Education and Welfare.
March 5, 1962. “Pollution of Waters of Puget Sound,
Strait of Juan de Fuca and Their Tributaries and Estuaries.”
Progress Report No. 1 of the Technical Coordinating
Committee. Washington, D.C.
United States Department of the Interior. March 1967. Pollu-
tional Effects of Pulp and Paper Mill Wastes in Puget
Sτund . Washington tate Enforcement Project. FWPCA,
Portland, Oregon. 474 pp.
United States Department of the Interior. July 1970. “Port
Angeles, Washington Water Quality Survey.” Survey #1.
Technical Assistance and Investigation; Office of Techni-
cal Programs. Seattle, Washington.
United States Environmental Protection Agency. 1972a. Unpub-
lished Survey. Port Angeles, Washington Water Quality
Survey #2. Surveillance and Analysis Division, Region X,
Seattle, Washington.
United States Environmental Protection Agency. l972b. Unpub-
lished Survey. Port Angeles, Washington Water Quality
Survey #3. Surveillance and Analysis Division, Region X,
Seattle, Washington.
211

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United States Environmental Protection Agency. December 1974.
“Evaluation of ITT Rayonier, Inc. Outfall Port Angeles
Harbor, Washington.” National Field Investigations Center -
Denver, Denver, Colorado. 100 pp.
United States Environmental Protection Agenc y. December 12,
1978. Storage and Retrieval (STORET) Data on Water
Quality Stations Monitored in the Port Angeles Area.
Raw Data Listing. EPA, Region X, Seattle, Washington.
Washington State Department of Ecology. 1972. Unpublished
Water Quality Data. Olympia, Washington.
Williams, R.W., W.M. Mains, W.E. E].dridge, and J.E. Lasater.
December 1953. Toxic Effects of Sulfite Waste Liquor on
Young Salmon . Research Bull in No. 1. Washington Depart-
ment of Fisheries. Olympia, Washington. 111 pp.
Young, S.R. and J.F. Cormack. August 2, 1976. “A Receiving
Water Survey of the Strait of Juan de Fuca Adjacent to
the Port Angeles Clarifier Outfall — June 1976.” Research
Memorandum No. 242 - 9. Crown Zellerbach Corp., Port
Angeles, Washington.
Ziebell, Charles D., R.E. Pine, A.D. Mills, and R.K. Cunningham.
1964. Unpublished Report. Field Bioassays and Salmon Fry
Distribution in Port Angeles Harbor, Washington. Washing-
ton Pollution Control Commission, Olympia, Washington.
212

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V. TOXICITY
Chapter II discussed the biologically toxic compounds of
bleached sulfite mill effluent (BSME) and effluent from
thermomechanical processes. A list of the BSME constituents
discharged by ITT Rayonier in Port Angeles has been shown in
Table 11-6. Data regarding the specific constituents of Crown
Zellerbach’s effluent is not complete; however, those compounds
which have been sampled are also shown in Table 11-6. Those
constituents thich are known or suspected of being toxic are
listed in Table 11—5. The purpose of this chapter is to dis-
cuss the impact of these toxic components on aquatic life.
Due to data availability, much of the discussion will be focus-
ed on ITT Rayonier.
The gross toxicity of BSME or thermomechanical effluent can
be measured on whole effluent as it is discharged from the mill
or specific toxicity of the individual components may be deter-
mined, provided that chemical separation is possible. The
gross toxicity of effluent discharged from the Port Angeles
mills has received some testing. Biomonitoring of the receiv-
ing waters has received considerable attention in the last two
decades by state agencies. This section of the report will
present a brief review of the recent literature on sulfite
effluent toxicity, gross toxicity bioassays of ITT Rayonier and
Crown Zellerbach effluent, receiving water bioassays and the
major known or suspected biologically toxic effects of effluent
components applicable to the ITT Rayonier mill in Port Angeles.
A. LITERATURE REVIEW OF SULFITE MILL EFFLUENT TOXICITY
The conventional ammonia base sulfite pulping process is used
by ITT Rayonier 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
213

-------
demand (BaD) 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 necessitates oxygenation to maintain adequate
oxygen levels for fish respiration 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.
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 any given plant, there are typically variations of
effluent constituents on a daily or hourly basis related to
mill operation changes. ITT Rayonier in particular changes
base compounds, types of wood used, and chemical additives
frequently due to the wide spectrum of products that they pro-
duce. 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 agents, etc., should be
known. The change in quantity and quality of the effluent in
a relatively short time period can alter the validity of toxic-
ity 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 V-A.
214

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100
40
Figure V—i.
ILLUSTRATION OF VARIABILITY BETWEEN PORT ANGELES
ALW BELLINGRAM SSL EFFJ CTS (BASED ON PERCENT
LARVAL ABNORMPiLITY IN OYSTERS)
Source: USD1 1967
S
80
60
-J
0
I-
IL l
C.)
U i
20
I I 1 1 I
010 20 30 40 50 60
SSL (ppml
I I I
80 100 120 140
215

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Recent 96-hour LC5O toxicity data reviewed by Hutchins (1979)
on whole sulfite—mill effluents (SHE), SSL and mechanical mill
effluent are included in Table V— I -. Data on both SME and SSL
are included because SSL contains most of the toxic constituents
present in whole effluent. The SSL stream is many times more
toxic than the whole SHE with the exception of bleaching ef flu-
ents. Inclusion of other process streams usually lowers the
toxicity of SSL (Wilson and Chappel 1973).
The 96-hour LC5O 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 ex-
pressed in mgi]. based on the Pearl Benson Index (PBI) which
is an indication of the amount of lignin present. The PBI is
limited in that it measures only a group of compounds that
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 LC5O values have been reported between 20
and 60 percent (Table V-i). Effluents from NH 4 —base mills are
usually not appreciably more toxic than those from Na—, Ca— or
Mg—base mills (Rosehart et al. 1974). However, effluent from
an NH 4 -base mill itilizing a bleach process was five times as
toxic as unbleached NH 4 —base sulfite effluent (Wilson and Chap—
pel 1973). Lagoon treatment lowered the toxicity of whole ef f—
luent (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
216

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Table V—i.
ACUTE EFFECTS OF SME, SSL AND MECHANICAL EFFLUENTS (ME) ON AQUATIC LIFE
Source: Hutchins 1979
Pacific salmon
Pacific salmon
Atlantic salmon
Atlantic salmon
Atlantic salmon
Pacific salmon
Pacific salmon
Rainbow trout
Rainbow trout
Rainbow trout
Rainbow trout
Atlantic salmon
Pacific salmon
Rainbow trout
Daphnia
Gammerus
Cyclops
Snail
2
3 — 45
25 — 60
11 — 24
15
0.7 — 1.45
2,340 mg/i (PBI)
3,000 mg/i (PRI)
0.18 — 0.29
1.1 — 3.5
8 — 12
2,500 mg/i (PBI)
1—2
25
14 — 18
18 — 32 (72 hr)
>100
>100
Untreated, Na and Ca base mills
Untreated Mg base
Untreated, Na base, high yield
Untreated, Na base, low yield
NH 4 base including bleachery wastes
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
Effluent
96-hr LC5O
Type Species
(7. by volume) Comments Reference
SHE
S SL
ME
Neutral sulfite semi—chemical process
Aged 5 days
Samples limited to red liquors, NH 4 base
Samples limited to red liquors, Mg base
Main sewer
Mixed hardwood and softwood marine water
Croundwood w/ small amount of kraft effluent
Groundwood W/ small amount of kraft effluent
Groundwood WI small amount of kraft effluent
Groundwood w/ small amount of kraft effluent
Groundwood w/ small amount of kraft effluent
Leach and Thakore 1974
Wilson 1975
Wilson 1975
Wilson 1975
Wilson 1975
Wilson 1975

-------
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 attri-
buted to conifer fibers, volatile reduced-sulfur compounds and
nonvolatile soluable 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 eff—
].uents, sublethal effects are expressed as a fraction of the
LC5O value for that organism. Sublethal effects of sulfite
wastes have received limited attention compared to kraft wastes,
while effects from mechanical mill effluent are not known.
The sublethal concentrations of SME and SSL reported in the lit-
erature usually have not been related to lethal concentration
as has been the case with kraft wastes. Therefore, sublethal
concentration of SME and SSL in Table V—2 are expressed as
either percent by volume or by the 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 SNE; however, the concentrations were not
given. In another paper he reported the production of green
algae was reduced by concentrations greater than 15 percent of
SME (Seppovaara and Hynninen 1970).
Gazdziauskaite (1971 a,b) studied the effects of SME on fresh-
water shrimp ( Pontogammarus) . He observed reduced growth at
1.5 percent, reduced reproduction at 3 — 12 percent and at
12 — 15 percent: increased respiration rate, reduced feeding,
218

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Effects
Respiratot y
Oxygen uptake
increased
Circulatory
Oxygen
reduced
tu
U,
Metabolism
Swimming ability
reduced
Behavior
Avoidance
Feeding reduced
Morphology, His tol y
Abnorinali ties
increased
‘S
Growth
Growth rate reduced
Eff. = Effluent
Gazd. = Gazdziauskaite
Table V-2. SUBLETHAL EFFECTS OF SULFITE MILL EFFLUENTS ON AQUATIC LIFE
Source: Hutchins 1979
Threshold Concentration
Fraction
Eff.
of 96—hr
Ό
Species Type
LC5O
Volume Comments Reference
Pontogammarus
SHE
———
12
LC independent of life stage
a,b
Salmonids
SSL
>1.0
100
Williams et al.1953
Rainbow trout
SHE
Abstracted article
Seppovaara 1973
Carp
SHE
Abstracted article
Seppovaara 1973
Pontogammarus
SHE
12 — 25
Increased respiratory quotient
Gazd. 1971 b
Pontagammarus
SHE
12 — 25
Abstracted article
Cazd. 1971 a,b
Salmonids
SSL
Avoid low but not high concen—
tration
Cazd. 1971 a,b
Pontagammarus
SME
12 — 25
LC5O independent of life stage
Gazd. 1971 a,b
Oyster larvae
SSL
———
6—12 mg/l
(PBI)
20% increase in abnormalities
Woelke 1960
Clam larvae
SSL
———
1—3 mg/i
(FBI)
20% increase in abnormalities
Woelke et al. 1970
Lyster larvae
SSL
———
0.15—0.5
Hg base most toxic (untreated
effluent)
Woelke et al. 1970
1972
Green algae
SHE
15
Abstracted article
Seppovaara &
Hynninen 1970
‘U

-------
behavior, reduced “blood values” and in some cases immobili-
zation. Growth was the most sensitive index. Although pro-
duction—abundance data are available for kraft mill effluents,
none were available for sulfite mill effluent.
The effect of SSL on oyster larvae ( Ostrea lurida and Crassos—
trea gigas) and clam larvae ( Tresus nutalli and Prototheca stami—
nea ) have received considerable study. These animals are quite
sensitive to SSL compared with salmonids (Stein et a].. 1959;
Woelke 1960a, b, c, d, 1965, 1976; Woelke et a].. 1970, 1972;
Cardwell et al. 1977a; Cardwell and Woelke 1979) and are
addressed in more det ail under receiving water bioassays.
Concentrations above 55 mg/i (PBI) inhibit spawning; however,
lower concentrations can stimulate spawning, but the resulting
larvae show a higher percentage of abnormality.
Larval Pacific oysters commonly develop abnormally within 48
hours in sulfite pu].pmill effluent concentrations less than
either 50 mg/i PBI or 0.05 to 0.2 percent effluent by volume
(USD1 1967 and Woelke 1965). Concentrations of sulfite pulp—
mill effluent causing 50% abnormal development in larvae
of horse clam ( Tresus capax and Tresus nutalii) , native little-
neck 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 combined
effects of pH change and ammonia toxicity.
Throughout this review little data has been found on the toxic-
ity of bleached sulfite mill effluent. Chlorine and chlorinated
compounds contribute the majority of toxicity in bleached kraft
220

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wastes, and it appears that a similar relationship may be
expected for sulfite mills. Evidence for this relationship
is discussed in Section D.3 at the end of this chapter.
B. GROSS TOXICITY BIOASSAYS
There are numerous procedures for monitoring the toxicity of
pulpmil]. effluents. The gross toxicity of pulp effluent can
be measured on whole effluent both before and after it is dis-
charged 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 subsections 3.1, B.2, B.3 respectively as they pertain
to Crown Zellerbach and ITT Rayonier mills in Port Angeles.
1. Crown Zellerbach Toxicity Bioassays
Methods: Crown Zellerbach Port Angeles mechanical pulping
mill effluent toxicity bioassays were conducted at their
EnvirOnniental Services Division (ESD), Carnas, Washington. The
methods utilized by ESD for toxicity tests appear to be some-
what ambiguous. No correspondence was found between DOE and
Crown Zellerbach that indicated which methods were to be imple-
mented by ESD. On August 13, 1974, Crown Zel] .erbach’s J.F.
Cormack advised adherence to DOE guidelines, but no Crown Zeller-
bach correspondence was found that acknowledged his advice.
In a letter from Watkins (letter to J.F. Cormack, June 7, 1977)
it was indicated that on May 27, 1977 bioassay methods recom-
mended by the California Fish and Game Department (Kopperdahi
1975) were used. Therefore Crown Zellerbach methods described
in this test have been determined from their raw bioassay data.
It appears that Crown Zellerbach followed DOE guidelines except
in the following cases. Diffused air was utilized until May 27,
1977; then the glass tube aeration method was employed. It is
221

-------
not certain if one or two controls were used per test series.
On May 7 1976 two control aquaria were used. But another
test data sheet (November 18, 1976) stated that two controls
had been used; however, only one control chamber was described.
All test dates except July 29, 1975 and December 25, 1977
stored the effluent samples beyond the DOE 48-hour limit. Test
temperatures reflected tap water temperatures of 7.8 — 15.80 C
and did not remain at the 15.0± 2.00 C DOE standard. These
temperatures probably would not alter test fish tolerances to
effluent; however, changes in chemical composition were likely
to occur.
Crown Zellerbach did appear to comply with DOE standards in
other aspects. For example, ten fish were used per test cham-
ber. The volume of test solution was increased when larger
fish were used to maintain the 1.0 g/l loading density limit.
Dechlorinated Camas city water was used for acclimation and
dilution water. Mortality during acclimation was documented,
as were test fish weights and lengths, test aquaria volumes,
water quality parameters (D.O. , pH, and temperature) for each
test solution vessel; and notes were taken on fish behavior.
Effluent samples were pH adjusted within DOE guidelines.
The Crown Zellerbach method of estimating the 96-hour LC5O
was the same as described in Standard Methods (APHA 1975).
Since a technique for determining an LC5O was not stipulated
this was justifiable. ESD used coho salmon ( Oncorhynchus
kisutch ) and rainbow trout ( Salmo gairdneri ) as test organisms
in accordance with DOE standards.
Re8ult8: The NPDES permit bioassay monitoring program for
Crown Zel].erbach was conducted from July 29, 1975 to December
5, 1977. The test dates, acute toxicity (96—hour LC5O), and
survival in 65 percent primary mechanical pulping effluent (ME)
222

-------
are given in Table V—3. The first noticeable change in
acute toxicity occurred on December 5, 1977 with a 96—hour
LC5O of >10 percent concentration while all prior tests had
LC5O’s ranging from <1.0 to <10.0 percent effluent concentra-
tion. An exact LC5O on the last test could not be determined
because only three effluent test solution concentrations at 1,
10 and 65 percent were tested. The higher survival was thought
to be due to the change in bioassay agents from zinc hydro—
sulfite to sodium hydrosulfite in July 1977. Zinc concentra-
tions in the effluent dropped radically from 800 mg/i on May
27, 1977 to 0.07 mg/i on December 5, 1977 (S.H. Watkins, letter
of December 13, 1977). The acute toxicity problem was alle-
viated subsequent to secondary treatment installation (Septem-
ber 1978). Bioassay results from secondary treated effluent
produced 100 percent survival in 65 percent and 100 percent
effluent concentrations for 96—hour test periods (C. Rock,
letter of May 24, 1978 and 3. Corniack, letters of December 14,
1978, May 23, 1979 and July 2, 1980), but prior to this survi-
val in 65% ME was zero.
The LC5O concentrations from tests conducted previous to May 27,
1977 could have been affected due to use of the diffused aera-
tion technique and extended effluent storage time. Tests on
April 20, 1976 and November 18, 1977 had greater than 10.0 per-
cent mortality in the controls (Table V-3). The DOE stated that
the acclimation mortality should not exceed 5 percent. The test
on August 14, 1975 exhibited a 9 percent acclimation mortality.
The control mortality criterion would disqualify acceptance of
these tests. Only the tests performed on rlay 27 and December
5, 1977 would be generally acceptable under DOE guidelines.
Crown Zel erbach Pilot Plant Studies: Crown Zellerbach had
no pilot plant bioassay studies, per Se, but in 1975 (Young 1975)
several tests were made to determine the toxicity of the eff-
luent (ME) during the mill’s trial run with a sodium hydrosulfite
223

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Table V-3. CROWN ZELLERBACH, PORT ANGELES, WASHINGTON, BIOASSAY DATA
Process: Mechanical Pulping Treatment: Primary Clarified (1972);
Specific Toxicant: Primary Effluent Secondary (September 1978)
SAMPLE
DATE
SAMPLE
TYPE
SPECIES X WEIGHT
TESTED (g)
LOADING
DENSITY
(g/l)
NO.
FISH/
TEST
TANK
CON-
TROL
MOR-
TALITY
(%)
96 HR.
LC 50
% CONC.
REFERENCES
7—29—75
N/A
Salmo gairdneri
0.8
0.80
10
0
<10.0
Chen 1977
8 _ 14 _ 75 a
N/A
S. gairdneri
0.9
0.90
10
0
52 a
Chen 1977
4—20—76
5—7—76
N/A
N/A
Oncorhynchus kisutch
0.38
0.38
0.92
0.92
10
10
20
0,0
2.6
3.4
Young 1975
Young 1975
0. kisutch
11—18—76
5—27—77
12—05—77
10-9-78
5-4-79
7-2-80
N/A
N/A
N/A
N/A
N/A
N/A
S. 9 irdneri
0.16
1.60
0.70
N.D.
0.88
N.D.
0.80
1.06
0.46
N.D.
N.D.
N.D.
10
10
10
10
10
10
10,0
0
0
N.D.
N.D.
N.D.
6.9
<1.0
>10.0
>65.0
>100.0
>100.0
Chen 1976
Hamblen &
Watkins 1977
H
Cormack 1978
Cormack 1979
Cormack 1980
S. irdneri
S. gairdneri
S. gairdneri
S. gairdneri
S. gairdneri
a 9.0% mortality in acclimation tank.

-------
bleaching agent. Effluent samples were collected in large
garbage cans, aerated with diffused air, and allowed to
cool at proper test temperatures. Coho salmon, tested at
the Port Angeles mill, averaged 88.0 nun in length. Guppies
( Lebistes reticulatus ) tested at ESD averaged 22.1 mm. Coho
salmon were tested in bioassays of 6 — 100% effluent while
guppies were tested in 65% effluent. Other methods followed
those of DOE standard methods.
Young (1975) found that coho salmon were more sensitive to
sodium hydrosu].fite ME than were guppies. Coho had an average
96-hour LC5O of 26 percent, while guppies exhibited a 96—hour
LC5O of 100% ME. Young’s data, however, may be somewhat mis-
leading due to the airstone aeration technique and having the
effluent exposed to air and light during cooling. These
factors create an environment for the reduction of effluent
toxicity. However, the toxicity of sodium hydrosulfite was
much lower than previous tests with zinc hydrosulfite bleaching
agents, which led to the use of the sodium process in 1977.
2. ITT Rayonier Toxicity Bioassays
Methods: ITT Rayonier Port Angeles sulfite pulpmill effluent
bioassay studies are believed to have been conducted at their
Hoodsport Laboratory. A letter on August 25, 1975 (F.C. Hawks,
letter of August 25, 1975) acknowledged that ITT Rayonier would
follow DOE standard methods. LC5O values were calculated using
a computer program. ITT Rayonier also used cliinethyl sulfoxide
(DMSO) as a reference toxicant to determine fish health.
Results: The ITT Rayonier NPDES permit toxicity bioassay tests
began in January 1976. The test dates, 96—hour LC5Q values,
and survival in 65% SHE are given in Table V-4. During most
tests ITT Rayonier failed to comply with many DOE specifications.
225

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Table V-4. ITT RAYONIER, PORT
ANGELES,
WASHINGTON
BIOASSAY
DATA
Process:
Sulfite
Treatment:
Primary
Clarified
Effluent
Specific
Toxicant:
Primary
Outfall
Dilution Source:
Fresh Water
SAMPLE
SAMPLE
SPECIES
LOADING
DATE
TYPE
TESTED
DENSITY
(g/ 1)
NO.
CONTROL
SURVIVAL
96HR.
FISH!
MORTAL-
IN
LC 50
TEST
ITY
65%
%
CONC.
TANK
(%)
EFFLUENT
REFERENCES
1—02-76
1—04—76
N.D.
Composite
.
Salmo
S.
gairdneri
gairdneri
N.D.
1.71
N.D.
10
N.D.
0,0
N.D.
0
37.5
39.97
Rogstad
1/2/76
Rogstad
1/29/76
8—16—76
Composite
S.
gairdneri
1.80
9
10,20
0
25.26
Rogstad
12/30/76
8—17—76
Composite
S.
gairdneri
1.80
9
10,20
0
23.78
Rogstad
12/30/76
12—06—76
GRAB
S.
gairdneri
0.48
9
10,20
0
25.21
Rogstad
12/30/7 6
, ,
‘ .4
°‘
1—03-77
6—29—77
N.D.
Composite
S.
S.
gairdneri
N.D.
0.33
N.D.
14
N.D.
20,20
N.D.
0
34.2
20.27
Rogstad
1/3/77
Rogstad
7/1 3/7 7
gairdneri
7—13-77
N.D.
S.
—
gairdneri
N.D.
N.D.
N.D.
N.D.
21.0
Rogstad
7/13/77
8—15—77
N.D.
S.
gairdneri
0.41
10
0,0
0
10.42
ITT Rayonier
8/15/7 7
7—12—78
N.D.
S.
gairdneri
N.D.
N.D.
N.D.
N.D.
31.5
Rogstad
7/1 2/7 8
12—13-78
N.D.
S.
gairdneri
N.D.
N.D.
N.D.
N.D.
5.6
Rogstad
4/30/79
1—24-79
N.D.
S.
gairdneri
N.D.
N.D.
N.D.
N.D.
4.5
Rogstad
4/30/79
5—24-79
N.D.
.
irdneri
N.D.
N.D.
N.D.
N.D.
33.0
Rogstad
12/17/79
11—29—79
N.D.
S.
gairdneri
N.D.
N.D.
N.D.
N.D.
100.0
Rogstad
N.D. = No Data

-------
Tests on August 16, 1976, August 17, 1976 and June 29, 1977
displayed control mortalities (Table V—4). In bioassays con-
ducted on August 16, 1976, August 17, 1976 and December 6, 1976,
the number of fish used per test aquarium was less than ten.
This was done to reduce the loading density when only larger
fish were available. Yet, using 6 or 7 fish instead of 10
reduced the statistical power (degrees of freedom) and deviated
from standard methods of the test. For three test dates (Jan-
uary 2, 1976, January 3, 1977 and July 13, 1977) no data ack-
nowledging the survival in 65% SNE were submitted to DOE. It
is not known if partial test values were submitted in error
or represent data from additional bioassays. Effluent sample
storage times were not listed except in one case (June 19,
1977). In this case, the effluent sample was collected and
stored beyond the 48-hour limit. There was no indication from
data in these files that the dilution water was tested to be
norktoxic to fish prior to experimentation. There was no data
previous to 1979 indicating changes in mill operations relat-
ing to changes in the toxicity of the effluent. All fish died
in all tests of 65 percent effluent. ITT Rayonier failed to
meet NPDES permit toxicity compliance of 100% survival in 65%
effluent. Deviations from prescribed bioassay methods (i.e.
loading density and high control mortality) make the validity
of these data subject to question. The test conducted August
15, 1977 is one of the few to follow prescribed standards.
ITT Rayonier Pilot Plant Studies: Following the installation
of secondary treatment, ITT Rayonier bioassay results improved
to the point that all fish survived in 100 percent effluent.
This was the first time that the 65% effluent limit was met or
surpassed. Toxicity studies were performed by ITT Rayonier
along with pilot plant studies of secondary treatment systems.
The tests were designed to determine the toxicity of primary
effluent treated via the secondary treatment processes of air
activated sludge (AAS), oxygen activated sludge (OAS), and
227

-------
rotating biological surfaces (RBS). Tests were conducted to
determine the 96—hour acute toxicity with rainbow trout. Since
the RBS tests were discontinued early in the study, data for
this processwere not available.
According to Denison and Samuelson (1975) the OAS and RBS
systems would not meet the State’s requirement of 100% survi-
val in 65% effluent (Table V—5). The average 96—hour LC5O
effluent concentrations for rainbow trout were 32.14, 82.9
and 55.34 percent for primary effluent, AAS and OAS treatment
systems, respectively.
These authors also concluded that the AAS system reduced
effluent toxicity and proved to be the most desirable means
of effluent treatment. Additional rainbow trout bioassay
were conducted in conjunction with the Washington Department
of Fisheries (Folson and Denison 1976) to determine the toxic-
ity of various effluents from the extended outfall (007) and
outfall (003A) with and without SWL recovery. These data
have been presented for comparison with oyster larvae bioassay
tests of effluent toxicity.
C. RECEIVING WATER BIOASSAYS
1. Live Box Studies
In the early 1960’s there was considerable debate over the
effects of pulp and paper mill effluent to the Harbor. Ziebe].l
et al. (1970) conducted a study in 1964 to determine the water
quality conditions and effects on sa] .monids within the Harbor.
Aside from visual and seine counts of fish in the polluted areas,
Ziebel]. et al. floated various mesh—enclosed cages in these
areas (live boxes) containing juvenile pink ( Oncorhynchus gor—
buscha ) and chum (0. keta ) salmon. The results showed that the
specific test areas were toxic to the salmon.
228

-------
Table V5. ITT RAYONIER BIOASSAY DATA
Source: Denison & Samuelson 1975
Process: Sulfite Treatment: Primary Clarified Effluent
Date Submitted: 6-6-75 Sample Type: Composite
UIOASSItY
NO.
REFER-
LOAUING
FISft/
CONTROL
96—HR
ENCE
TEST
PROCESS
SPECIFIC
SPECIES
i
WEIGHT
(g)
DENSITY
TEST
I’IORTAL1TY
LC 50
NUMBER
DATE
GRADE
TOXICANT
TESTED
(g/L)
TANK
(%)
(%CONC.)
A-24 2-04-75 Nitration Primacy Saimo gairdrieri N/A N/A N/A N/A 39.0
Effluent
A-26 2-05-75 Paper N/A N/A N/A N/A 46.5
A-29 2-09-75 Paper “ N/A N/A N/A N/A 45.5
A-32 2-12—75 Acetate H N/A N/A N/A N/A 22.5
A-36 2-16-75 Ace te “ N/A N/A N/A N/A 28.0
A—39 2-19—75 Acetate 0 1.26 0.63 5 0,0 22.2
A-43 2-23—75 Ace te H/A N/A N/A N/A 17.0
A—46 2—26—75 Acetate I’ 1.90 1.91) 10 0,0 35.2
A-50 3-02—75 Acetate 1.90 1.90 10 0,0 36.6
A—53 3—05—75 Acetate 1.79 1.79 10 0,0 39.8
t..., A-58 3-10—75 Acetate 1.79 1.79 10 0,0 34.8
A-61 3-13-75 Acetate “ N/A N/A N/A N/A 36.8
A-64 3-16—75 Nitration N/A N/A N/A N/A --
A—67 3—19—75 Acetate 2.38 1.67 7 0,0 30.9
A—7] 3—23—75 Acetate 2.38 1.67 7 0,0 24.7
A-74 3—26—75 Paper 2.83 1.70 6 0,0 36.3
A-78 3—30—75 Paper “ 2.83 1.70 6 0,0 36.3
A-B]. 4-02—75 Acetate t!/A N/A N/A 0,0 28.0
A-85 4—06—75 Acetate 1.50 1.50 10 0,0 17.5
A—8 8 4—10—75 Mill IS “ 1.55 1.55 10 0,0 33.4
Shutdown
A—91 4—13—75 Mill 1.55 1.55 10 0,0 31.7
Shtitdown
T-24 2-04-75 Nitration Aerated Acti- N/A N/A N/A N/A 64.0
vated Sludge
T—26 2—05—75 Paper “ 1.36 0.68 5 0,0 63.5
T-29 2-09-75 Paper N/A N/A N/A N/A 68.0
T-32 2-12—75 Atetate N/A N/A N/A N/A 51.5
T-36 2-16-75 Acetate 0 N/A N/A N/A N/A 51.0
T-39 2-19-75 Acetate ‘I N/A N/A N/A N/A >70.0

-------
Table V-5 Continued Page 2.
Process: Sulfite Treatment: Primary Clarified Effluent
Date submitted: 6-6-75 Sample Type: Composite
BIOASSAY
no.
REFER-
LOADING
F131/
CONTROL
96-HR
ENCE
TEST
PROCESS
SPECIFIC
SPECIES
x
WEIGHT
(g)
DENSITY
TEST
MORTALITY
LC 50
NIUIBER
DATE
GRADE
TOXICANT
TESTED
(g/L)
TANK
(%)
(%CONC.)
T—43 2—23-75 Acetate Aerated Acti— Salino gairdneri 1.26 0.63 5 0,0 50.9
vated S1u 1ge
T—46 2—26—75 Acetate U “ 1.90 1.90 10 0,0 78.7
T-50 3-02-75 Acetate U U N/A N/A N/A N,’A ‘79.0
T-53 3-05-75 Acetate “ N/A N/A N/A N/A >88.0
T-58 3-10—75 Acetate “ “ N/A N/A N/A N/A >88.0
T-61 3-13—75 Acetate “ “ N/A N/A N/A N/A >100
T-64 3-16—75 flitration “ U N/A N/A N/A N/A >100
3-19-75 Acetate “ SS N/A N/A N/A N/A >100
T-71 3—23—75 Acetate “ hI N/A N/k N/A N/A >100
T-74 3-26-75 Paper “ “ N/A N/A N/. N/A >100
J T-78 3-30-75 Paper “ N/k N/A N/A N/A >100
o T-81 4-02-75 Acetate “ “ N/A N/A N/A N/A ‘ ‘88.0
T-85 4-06-75 Acetate U N/A N/A N/A N/A >100
T-88 4-10-75 Mill Shutdown “ “ N/A N/A N/A N/A >100
T-91 4-13-75 Mill Shutdown “ “ N/A N/A N/A N/A >100
B-24 2—04-75 Nitration Oxygen-Aeration U N/A N/A N/A N/A 57.5
Activated
Sludge
B-26 2-05-75 Papei. “ N/A N/A N/A N/A 48.0
B—29 2-09—75 Paper .1 ‘ 1.36 0.68 5 0,0 57.0
13-32 2-12-75 Ace late N/A N/A N/A N/A 36.0
13-.’6 2-16-75 Acetate “ N/A N/A N/A N/A 55.0
B—39 2—19—75 Acetate “ 1.26 3.63 5 0,0 64.8
8-43 2—23—75 Acetate 1.26 0.63 5 0,0 42.0
B—46 2—26—75 Acetate “ 1.90 1.90 10 0,0 57.5
8—50 3—02—75 Acetate “ 0 1.90 1.90 10 0,0 64.8
fl—53 3—05—75 Acetate U N 1.79 1.79 10 0,0 54.5
B—58 3—10—75 Ace late ‘I “ 1.79 1.79 10 0,0 37.9
8—61 3—13—75 Acetate “ “ 1.96 1.57 8 0,0 39.8

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Table V5 Continued Page 3.
Process: Sulfite Treatment: Primary Clarified Effluent
Date Submitted: 6-6-75 Sample Type: Composite
EIOPSSAY
NO.
REFER-
LOADING
FISH!
CONTROL
96-HR
ENCE
TEST
PROCESS
SPECiFIC
SPECIES
x WEIGHT (g)
DENSITY
TEST
MORTALITY
LC 50
NUMBER
DATE
GRADE
TOXICANT
TLS ’ ED
(g/L)
TANK
(%)
(%CONC.)
B-64 3—16-75 Nitration Oxygen—Aeration Salmo irdneri 1.96 1.57 8 0,0 49.8
Activated
Sludge
B—67 3—19-75 Acetate 2.39 1.67 7 0,0 05.1
8-71 3 23-75 Acetate “ N/A N/A N/A N/A >79.0
B—74 3—26-75 Paper “ ‘S 2.83 1.70 6 0,0 76.6
B-78 3-30-75 Paper “ N/A ti/A N/A N/A N/A
13-81 4—02-75 Acetate “ 1.50 1.50 10 0,0 38.5
8-85 4—06-75 Acetate “ “ 1.50 1.50 10 0,0 39.2
B-88 4—10-75 Miii Shutdown “ “ N,’A N/A N/A N/A 83.0
B—91 4-13—75 Miii Shutdown “ “ 1.55 1.55 10 0,0 60.8

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The major problem of live box field bioassays is that they
are not specific enough to the pollutant source in question.
The test organisms in live boxes can be exposed to a number
of pollutants (i.e. oil, grease, sewage, etc.) other than the
effluent or point source under investigation. In addition, the
responses of the test specimens are very difficult to observe
in live box studies and there is no control of the environ-
mental conditions under which such tests are conducted.
2. Oyster Larvae Bioassays
A widely used organism for receiving water bioassays in the
marine waters of Washington State is the larvae of the Pacific
oyster ( Crassostrea gigas ) (Cardwel]. and Woelke 1979). The
Pacific oyster was chosen because the species is commercially
important, sensitive to low concentrations of pulpmi].l efflu-
ents (Gunter and McKee 1960; Woelke l960a) and amenable to
standard testing in the laboratory (Woelke 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
are referenced to the following selected water quality para-
meters: Pearl Benson Index (PBI), salinity and age of the
seawater sample at the time testing commenced. A review of th
specific procedures and considerations of the oyster larvae
bioassay is contained in Appendix V-B.
The receiving water biomonitoring responses for the Port
Angeles region have been presented for the period 1961 - 1976
by Cardwell and Woelke (1979). Additional unpublished data
for 1977 and 1978 were supplied by Cardwell. Bioassay of sam-
ples 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 the salinity falls below
the 20% threshold determined by Woelke (1968). However, the
salinity rarely fell below this limit in Port Angeles receiving
waters.
232

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D. MAJOR EFFLUENT COMPOUNDS AND ORGANISM RESPONSE
1. Introduction
Isolating the individual constituents of mill effluent and
determining their toxic nature is valuable in the sense that
a general knowledge of the components responsible for the
toxic response 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.
Due to data availability, discussions in the subsections below
focus on bleached sulfite mill effluent. The toxicity of
BSME components are measured using bioassay procedures simi-
lar to those used in assaying whole BSNE. The studies pre-
sented below represent the responses of a wide variety of
aquatic life to BSME.
2. Organic Acids 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). Hutchins has stated that resin acids
are the primary toxic contributor in mechanical mill effluent.
Abietic, dehydroabietic, isopimaric, palustric, and pimaric
acids all cause toxic responses with LC5Q levels ranging from
.22 — .75 mg/i (Hutchins 1979).
The compounds and their associated toxicities are presented in
Table V—6 for sulfite mills. Similar compounds are generally
present in mechanical mills; however their concentration in the
waste streams are generally less (Hutchins 1979). Resin acids
233

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Table V—6 MAJOR COMPOUNDS IDENTIFIED IN SULFITE PULPING OPERATIONS WHICH ARE TOXIC TO FISH MID INVERTEBRATES
Deterpene Alcohols
Pimarol
Isopimarol
Dehydroabietol
Abietol
Juvabiones
Juvabione
Juvabiol
A” • -Dehydrojuvabione
Dehydrojuvabione
Rainbow Juvenile 0.3
• • 0.3
• • 0.8
N •• 1.8
1
1
1
1
1
1
1
1
20 ——— Metabolism — inability of SW acclimated smolta
to adapt to F.W.
Sockeye 20 --— Morphology - lW acclimated smolta*
edema, bloating of gut
Sockeye M.D. —-— Morphology - SW acclimated smelts;
loss of water from muscle tissue
Sockeye N.D. —-— Metabolism - high accumulation in viscera (pg/g)
brain6l9.8, kidnay 27B. 1, liver262.5
Rainbow M.D. —-— Metabolism - high accumulation in viscera (Iig/g)
brainl54.3 , kidneyNl82.5 , liverN29O.6
Estuarine M.D. ——— Metabolism - 25 mg/I accumulation in tissues
amphipods
Species
Species
96-hr
LCSO
Fraction
of
96-hr
Chemical Tested
size
(g)
(mci/I) Sublethal
Response LC5O Conunents Reference
Resin Acids
Abietic
Coho
Rainbow
0.2-0.75
Juvenile
0.41
0.7
Dyhydroabietic
Coho
Rainbow
0.2-0.75
Juvenile
0.75
1.1
Isopimaric
Coho
Rainbow
0.2-0.75
Juvenile
0.22
0.4
Pimaric
Coho
Rainbow
0.2-0.75
Juvenile
0.32
0.8
Sandaracopimaric
Coho
0.2-0.75
0.36
Static
with 4-8
hr replacement
1
Static
without
replacement
1
Static
with 4—8
hr replacement
1
Static
without
replacement
1
Static
with 4-0
hr replacement
1
Static
without
replacement
1
Static
with 4—8
hr replacement
1
Static
without
replacement
1
Static
with 4-8
hr replacement
1
Static
without
replacement
N
N
N
Long-Chain Fatty Acids
Dehydroabietic acid (RA) Sockeye
• N N
N N N
Rainbow
Juvenile
1.5
Static with 4 hr
replacement
N
N
18
N
•
•
0.8
N
N
N
2.0
N
N
0.65 mg/l Suggests inhibition of osmaregu-
lat ion
0.65 mg/l Suggests osmotic imbalance
0.65 mg/I Suggestes osmotic imbalance
0.65 mg/l Freshwater, S day exposure
Continuous flow bioassay
0.65 mg/i Freshwater, 5 day exposure
Continuous flow bioassay
0.65 mg/I Freshwater. 5 day exposure
Continuous flow bioassay
2
3
3
3
3
3
References; 1 Leach & Thakore 1977
2 DavLs 1976 3 Kruzynski 1979

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are the primary toxic components found in softwood pulping
waste streams in Canada. The individual acids had 96—hour
LC5O’s for coho salmon of 0.2 — 0.75 mg/i in static bio—
assays with 4 — 8 hour solution replacement. Tests with
juvenile rainbow trout without replacement resulted in 96—hour
LC5O’s of 0.4 — 1.1 mg/i. A marked increase in resin acid
toxicity occurred with decreasing pH in the range of 7.5 — 6.4.
The diterpene alcohols were found in trace quantities with
96—hour LC5Q’s ranging from 03 - 1.8 mg/i. Several naturally
occurring insect juvenile hormone mimics related to juvabione
had 96-hour LC5O’s ranging from 0.8 — 2.0 mg/i for rainbow
trout. Leach and Thakore (1977) found that secondary treat-
ment reduced or eliminated the toxicity of most of these
chemicals; however, some do not readily degrade and remain
toxic. It should be noted that these tests have all been con-
ducted in freshwater. Discharge of organic pulping compounds
into marine receiving waters may result in more rapid reduc-
tion in the toxicity in the mixing zone than occurs in fresh-
water.
The literature on sublethal effects of sulfite and mechanical
effluents compounds is quite limited. Data found for sublethal
effects are limited to dehydroabietic acid (Table V.-6). Davis
(1976) conducted a study on sockeye salmon acclimated to sea-
water and exposed to 0.65 mg/i dehydroabietic acid and found
some indication of osmoregulatory inhibition. Kruzynski (un-
published 1979) found that freshwater acclimated sockeye salmon
in 0.65 mg/i dehydroabietiC acid accumulated water in the muscle
tissues (edema) and there was bloating of the gut. Saltwater
acclimated chum salmon (0. keta), on the other hand, developed
a high loss of water from muscle tissue. Both of these tests
suggest osmotic imbalance due to the resin acid. In more re-
cent studies (Kruzynski 1979) various aquatic species
were exposed to 0.65 mg/i dehydroabietic acid for five
235

-------
days in a continuous flow through a bioassay chamber. Extreme-
ly high accumulations of this compound were found in the
viscera and tissues. This indicated that dehydroabietic acid
is highly water soluble and deposits quickly in the blood
and lipid layers of the sa].monids. High concentrations were
also found in the bile of sockeye salmon and rainbow trout.
Estuarine amphipods exposed to 0.65 mg/l of dehydroabietic
acid had 38 times that amount in their tissue. This suggests
that a bioaccumu].ation of this toxicant in the food chain may
result.
Chemical identification of similar effluent components has
not been made for either the Crown Zeilerbach or ITT Rayonier
mills. Analytical testing has generally been limited to a few
tests on the toxicity of defoamers, slimacides, dyes and trace
metals which result from addition to various stages of the pulp-
ing process. Young (1975) performed a series of chemical tests
to determine toxicities of various components and additives.
His methods are described in the pilot plant tests described
for Crown Zel].erbach. Results of his findings were:
Concentration
Chemical Tested in Effluent LC5O (mg/i )
Defoamer (Nalco 129) 5 mg/i 5.0
Dye (Calcozine FXW—yellow) 18 mg/i 3.2
Slimacide (Cytox 3522) 8.9 mg/i 1.3
Copper 0.05 — 0.10 mg/i 0.026
Lead 0.01 — 0.06 mg/i 0.04
Zinc 1.07 mg/i 0.8
Groundwood solubles 16%, 65% eff.
Young states “the possibility of groundwood solubles being
responsible for the toxicity has been eliminated because
higher levels than those present in the effluent were not
toxic. Resin acids show no apparent relation to toxicity.”
236

-------
This statement can be quite misleading because of the bioassay
methods used. In effect, his aeration method (diffused air)
would be similar to secondary treatment (i.e. aerated lagoon).
Groundwood solubles tested include only the resin acids:
pimaric acid (7.2 mg/i), isopimaric acid (0.6 mg/i), abietic
acid (1.6 mg/i) and dehydroabietic acid (6.7 mg/i). Literature
from Leach and Thakore (1977) have shown that these chemicals
are t xic to rainbow trout and coho salmon.
ITT Rayonier toxic constituent tests produced the following
results:
Chemical 96—hour LC5O (mg/i )
Acetaidehyde 115
Formic acid 550
Acetic acid 3000
p—Cyniene 44
Furfural 18
5—Methylfurfura]. 61
Guaiacol 100
Eugeno]. 11.5
Isoeugenol 9.9
The toxicities reported appear to be very low; however, none of
the chemicals tested in the Crown Zellerbach or ITT Rayonier
effluents are directly comparable to the results of Leach and
Thakore (1977) either due to the difference in testing method
utilized or the dissimilarity of the chemicals.
3. Bleach and Related Compounds
Enormous quantities of pulp are bleached in the manufacture of
paper. Sulfite pulps are usually bleached by the CEN multi-
stage process (chlorination, alkaline extraction and hypochior-
ite stages). The chlorination stage delignifies the pulp by
237

-------
forming chiorolignin compounds which are subsequently removed
in the alkaline extraction stage. The pulp is then bleached
or brightened during the final hypochiorite stage. The bleach
waters are then discharged along with the sulfite mill effluent.
Concern regarding the environmental effects of discharging
chlorine and chlorine by—products to fresh and marine waters
has led to an increase in the amount of scientific investiga-
tions in the last 10 years. The toxicity of chlorine in fresh-
water has received extensive investigation; however, it has
been only recently that the problem of chioro-orgaflics with
potential health and environmental effects has been identified.
The chemistry of chlorine in seawater has recently been recog-
nized 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 ecosys-
tems.
The bromide ion in seawater has been shown to play a major role
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, chioramines, brorna—
mines, etc.). Sugam and Helz (1977) have recently proposed a
sequence of reactions for chlorine degradation in a marine en-
vironment (Figure V—2). The actual reaction products formed
during the conversion of one oxidant into another are dependent
upon several variables, among which are pH, salinity (amount
of 8r), ammonia nitrogen, chlorine dose, and temperature
(Helz et al. 1978)
The importance of ammonia nitrogen concentration in the chemis—
try of chlorinated seawater and its toxicological implications
has been examined by Inmann and Johnson (1978). In full—
strength chlorinated seawatez broinaxnines may be formed from the
hypobromous acid resulting from bromide hydrolysis at low
238

-------
Cl 2
HOd +H +Cl
4
HOC1 4 )-OCI+ H
NH 2 CI. NHCI 2 ,
ORGANIcS
CHLORO -ORGANICS
DEGRATION to Cl -
NH 3
ORGANICS
NH 2 BF, NhSc 2 , NB , 3
I BROMO-ORGANICS I
1
DEGRADATION TO Br
Figure V-2. PROPOSED SEQUENCE OF REACTIONS FOR THE DEGRADATION
OF CHLORINE IN AQUATIC SYSTEMS.
Reactions of HOd and HOBr with inorgainic reducing
agents have been omitted because they are probably
of negligible importance in most cases.
Source: Sugam and Helz 1977.
/
MCI 3
NH 3
+
ORG 4
HOar - 4 OBr+ H
1
L
I
ORGANICS
/
239

-------
ammonia nitrogen concentrations. The degree of halogen sub-
stitution on nitrogen will be determined by pH and the hal-
ogen ammonia ratio (Johnson and Overby 1971).
For ammonia nitrogen level less than 0.4 mg/i, pH at 8.1, and
sufficiently large chlorine doses, tribromaznine and hypo—
bromous acid are the major products. When the ammonia nitro-
gen level is greater than 0.5 mg/i and the chlorine dose is
less than 2.5 mg/i, monochioramine competes with bromide
oxidation and a ha].oamine mixture of monochioramine and di—
bromamine results. At even greater ammonia concentrations
and longer time, monochloramine becomes the predominant oxi-
dant 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 monochioramine 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 mono—
chloraxnine may be present as part of the total oxidant concen-
tration in sufficient amounts to exert a toxic effect on var-
ious forms of marine life. At present there is inadequate
analytical methodology for the estimation of low concentra-
tions (<1 ug/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
affect the toxicity of chlorine to marine organisms (Table V-7).
These included concentration, exposure time, temperature, chem-
ical species of chlorine and biotic factors such as species,
life stage and size of organism. In addition, other environ-
mental factors such as pH and metal pollutants (copper arid
nickel) modify toxicity; however the two factors of most impor-
tance in the determination of toxicity are concentration and
240

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Table V-i TOXICITY OF CHLORINE TO MARINE ORGANISMS IN PUGET SOUND AND ADJACENT WATERS SELECTED FROM:
CRUMLEY, STOBER AND DINNEL 1980.
Test Test Concentra—
Organism Conditions 1 tion (ppm) 2 Remarks References
MOLLUSCA
Crassostrea CB, SW, LS 0.44 (Amp) 48 hr EC5O; 10 day larvae Thatcher et al. 1976
gigas
ARTIIROPODA-
CRUSTACEA
Anonyx sp. CB, SW, LS 0.145 (Pmp) 96—hr LC5O, 10°C acclimation temp; 14.8°C Thatcher 1978
exposure temp; salinity 18 °/ ,, ; pH 8
Crangon CB, SW, LS 0.134 (Amp) 96—hr LC5O; 10°C acclimation temp.; 14.8°C Thatcher 1978
nigricauda exposure temp.; salinity 28 0/co ; pH 8
Hemigrapsus CB, SW, LS 1.418 (Amp) 96—hr LC5O, 10°C acclimation temp.; 14.8°C Thatcher 1978
nudus , H. exposure temp.; salinity 28 °/ €, ; pH 8
oregonensis
Neomysis sp. CB, SW, LS 0.162 (Amp) 96—hr LC5O; 10°C acclimation temp.; 14.8°C Thatcher 1978
exposure temp; salinity 28 0/co ; pH 8
Pandalus CS, SW, LS 0.210 (Amp) 96-hr LC5O; 15°C Thatcher et al. 1976
danae 0.20 Hatching of eggs inhibited in 6—day test
Pandalus CB, SW, LS 0.090 (Amp) 96—hr LC5O; 10°C acclimation temp.; 14.8°C Thatcher 1978
goniurus exposure temp.; salinity 28 °/co ; p11 8
Pontogenia CB, SW, LS 0.687 (Amp) 96—hr LC5O; 10°C acclimation temp.; 14.8°C Thatcher 1978
sp. exposure temp.; salinity 28 °/ , ; pH 8
CLUPEIDAE— herrings
Clupea harengus 96-hr LC5O; 10°C acclimation temp.; 14.8°C Thatcher 1978
pallasi CS, SW, LS 0.057 (Amp) exposure temp.; salinity 28 °/co ; pH 8
Continued.

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Table V—7 Page 2.
> 0.023
< 0.052 (Amp)
0.5 (0T)
0.25
0.10
0.208 (Amp)
0.130
0.142
0.002-0.5
0.032 (Amp)
> 0.038
< 0.065 (Amp)
0.5 (oT)
0.25
0.05
Test
Concentra—
Conditions’
tion
(ppm) 2 Remarks References
Test
Organism
SALMON IDAE -
Trout and Salmon
Oncorhynchus CB, SW, LS
gorbuscha
0. gorbuscha CB, SW, LS
0. kisutch CB, SW, LS
0. kisutch CB, SW, I,S
0. tshawytscha CB, SW, LS
0. tshawytscha CB, SW, LS
GASTEROSTEIDAE -
Sticklebacks
Gasterosteus C8, SW, LS
aculeatus
96—hr LC5O; 10°C acclimation temp.; 14.8°C
exposure temp.; salinity o/ ,, , p118
7.5 mm. LC5O, salinity 20 - 26 O/ ,, ;
pH 7.23 — 7.80
60 mih LC5O
60 mm LC5O, +9.9°C temp. shock
60 mm LC5O, 12.7°C, pH 7.8, salinity 29.6 O/ ,
60 mm LC5O; 12.7°C +7.3 C°temp. shock, pH 8;
salinity 28.8 °/ ,
24—hr LC5O; 12.1°C temp.; pH 7.9; salinity
29.4 °
avoidance, 12°C
96—hr LC5O; 10°C acclimation temp.; 14.8°C
exposure temp.; salinity 28 % ,; pH 8
96-hr LC5O; 10°C acclimation temp.; 14.8°C
exposure temp; salinity 28 , p11 8
15 mm LC5O; salinity 20-28 % ; pH 7.66-7.83
60 mm LC5O
60 mm LC5O, +10°C temp. shock
96-hr LC5O; 10°C acclimation temp; 14.8°C
exposure temp.; salinity 28 °/ , pH 8
Continued.
Thatcher 1978
Stober & Hanson
1974
Stober et al. 1980
Thatcher 1978
Thatcher 1978
Stober & Hanson 1974
Thatcher 1978
0.167

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Table V—i Page 3.
Test Test
Organism Conditions 1
Concentra—
tion (ppm) 2
Remarks
References
EMBIOTOCIDAIE-
Surf perches
Cymatogaster CB,
aggregata
SW,
IS
0.2 (Amp)
0.301
1.0
0.175-0.5
No mortality. 60 mm. exposure.
60 mi LC5O; 13°C; pH 8.1
100% mortality
avoidance ; 12°C
Stober et al. 1980
C. aggretaga CB,
SW,
IS
0.071 (Amp)
96-hr LC5O; 10°C acclimation temp.;
exposure temp.; salinity 28 O/ ; pJj
14.8°C
B
Thatcher 1978
AMMODYTI DAE-
Sandlances
Ammodytes CB,
hexapterus
SW,
LW
0.082 (Amp)
96-hr LC5O ; 10°C acclimation temp.;
exposure temp.; salinity 28 .1 ; pH
14.8°C
8
Thatcher et al. 1976
PLEURONECTI DI E-
Right—eye flounders
Paroph!y! CB,
vetulus
SW,
LW
0.073 (Amp)
96-hr LC5O; 10°C acclimation temp.;
exposure temp.; salinity 28 °/ ,,pH 8
14.8°C
Thatcher 1978
1. SB static bioassay, CB = constant flow bioassay, SW = saltwater, FW = freshwater, LS = lab study
FS = field study
2. Amp = amperometric tritration, OT = acid orthotolodine

-------
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 result-
ing 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, juve-
nile, adult), size, and species specific sensitivity appear
to influence toxicity.
Thatcher (1978) conducted a series of 96—hour LCSO continuous—
f low bioassays to determine the impact of chlorination on 15
estuarine and marine fish and invertebrates common to Puget
Sound and adjacent waters (Table v-7). A thermal stress was
included and total residual oxidant (TRO) concentrations were
measured by amperometric titration. In general, the fishes
were more sensitive than the invertebrates. Based on LC5O
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
herring, shiner perch, English sole, Pacific sand lance, and
a shrimp ( Panda].us goniurus) . The 96-hour LC5O values for
this group were 0.026 to 0.119 mg/i TRO. The group of inter-
mediate sensitivity included the shrimp ( Crangon nigricauda) ,
the amphipod ( Axnmyx sp.), the mysid ( Neomysis sp.), the three—
spine stickieback ( Gasterosteus aculeatus ) and the coon stripe
shrimp ( Pandalus danae) . Their 96-hour LC5O values ranged from
0.118 to 0.199 mg/i. The most resistant group consisted of the
axnphipod ( Pontogeneia sp.) and the shore crabs ( Hemigrapsus
nudus and H. oregonesis) . Their 96—hour LC5O values ranged
from 0 .583 to 1.530 mg/i TRO.
244

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Comparing two species in seawater, Stober et al. (1980) found
that coho salmon ( Oncorhychus kisutch ) proved to be more
sensitive to TRO than shiner perch ( Cyinatogaster aggregata )
with a 24—hour LC5O of 0.123 mg/i for shiner perch approxi-
mating a 12—hour LC5O for coho salmon of 0.114 mg/i (Table
V-7). Coho salmon were also significantly more sensitive to
chlorinated seawater for short exposure times of 7.5, 15, 30
and 60 minutes than shiner perch. A three—way matrix test
design with chlorine concentration, exposure time and temper-
ature as test variables was used. Exposures of 60 minutes or
less to shiner perch produced no mortalities in concentrations
less than 0.2 mg/i TRO, although increased respiration rates
indicated a response to chlorinated seawater at levels of 0.10
mg/i. TRO concentrations of more than 1.0 mg/i 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 tempera-
ture shock of +7C (but not at +3C). Coho salmon experienced
no mortality below 0.10 mg/i TRO for the range of exposures
and temperatures tested, while 100 percent mortality was
observed at concentrations greater than 0.50 mg/i TRO. A temp-
erature shock of +7C resulted in a significant decline in LC5O
values from exposure times of 7.5, 15 and 30 minutes. A +3C
temperature shock above ambient had no significant effect.
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 temp-
eratures (Table V—7 ). Temperature increases of 9.9 to 1OC
above acclimation and 0.5 mg/i 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
245

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of chlorinated water, the toxic effects in the field could
approximate 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 res-
ponses (avoidance or attraction) become important when con-
sidering 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 ugh
TRO and was reinforced with increased temperature. Shiner
perch avoided TRO at 175 ugh, while a significant preference
response at 16C and 20C occurred at 10, 25, 50 and 100 ugh.
Thatcher (1978) determined that the 96—hour LC5O for shiner
perch in chlorinated seawater was 71 ugh TRO and consequently,
continuous discharges of heated seawater having a chlorine
TRO of 71 — 100 ug/l could attract shiner perch and eventually
result in adverse sublethal effects.
Crown Zellerbach uses the sodium—hydrosulfite based Ventron
process to lighten their pulp and paper. ITT Rayonier, however,
still uses chlorine based bleaching agents. Although EPA
acknowledges that considerable amounts of chlorine are used
(Bodien, personal communication), ITT Rayonier is not required
to report residual chlorine discharged. Therefore chlorine
discharge levels are not known.
4. Sludge Beds
In the late 1960’s sludge bed toxicity was strongly debated.
Sludge beds are the accumulations of discharged settled un-
treated primary effluent. This highly glassine substance
246

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does not degrade very rapidly but produces a moderately high
concentration of hydrogen sulfite, especially at low tides.
The Washington State Water Pollution Control Commission (now
the DOE) wanted the sludge beds removed from Port Angeles
Harbor. Crown Zellerbach studies by Aspitarte and Smale
(1972) concluded that the sludge beds were decomposing yet
stabilized. The authors wariled that if the sludge beds were
to be removed, hydrogen sulfide and resuspension of the solids
would occur posing greater toxic threats to the Port Angeles
Harbor. Thus, after 1963, the issue of sludge bed removal was
shelved.
247

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REFERENCES
CHAPTER V
American Public Health Association (APHA), American Water Works
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Aspitarte, T.R. and B.C. Smale. 1972. “Sludge Bed Survey
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Cardwell, R.D., C.E. Woelke, M.I. Carr, and E.W. Sanborn. 1977a.
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Cardwell, R.D. and C.E. Woelke. 1979. Marine Water Quality
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Chen, H.T. November 26, 1976. Letter to J.F. Cormack.
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Davis, J.C. 1976. “Progression Sublethal Effect Studies with
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Denison, J.G. and C.E. Samuelson. 1975. Toxicity Analysis
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Folson, M.W. and J.G. Denison. 1976. Port Angeles Division
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State Department of Fisheries . Unpublished. January 8,
1976.
Gazdziauskaite, I.B. 1971a. “Effects of Effluents from the
Sovetsk and Neman mills on the biology of Pontoganunarus
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Liet. TSR Mokslu. Adad. Darbai . Ser. C. No. 2:93.
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Gazdziauskaite, I.B. 197lb. “Effect of Effluents from the
Sovetsk and Neman Sulfite Pulp Mills on the Fertility
of Pontogammarus robustoides (Grimm) sars.” Rybokhoz.
Isuch. Vnutr. Vodoeiρ r No. 6:29-31. (Ab. BulI Inst. Paper
Chemistry 43:3026).
Grande, M. 1964. “Water Pollution Studies in the River Otra,
Norway - Effects of Pulp and Paper Mill Waste on Fish.”
mt. J. Air Wat. Pollut . 8:77.
Gunter, G. and J.W. McKee. 1960. On Oysters and Sulfite Waste
Liquor . Washington Water Pollution Control Conimisison.
Iympia , Washington. 93pp.
Hainb].en, and S.H. Watkins. 1977. Static Bioassay Worksheet.
Crown Ze].lerbach Corp. (Dec. 5), Port Angeles, Washington.
Hawks, F.C. August 25, 1975. Letter to James C. Knudson.
Central Operations Division. DOE. Olympia, Washington.
Helz, G.R., R. Sugain, 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.
Hutchins, F.E. 1979. Toxicity of Pulp and Papermull Effluents -
A Literature Review . EPA-600/3-79-0l3. 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
!fects . (R.J. Jolley, H. Gorchev and D.H. Hamilton, eds.)
Ann Arbor Science Vol I. pp 235—252.
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ITT Rayonier, Inc. August 15, 1977. Bioassay Results.
Form ORD 3105C.
Johnson, J.D. and R. Overby. 1971. “Bromine and Bromine
Disinfection Chemistry.” J. San. Eng. Div. Am. Soc. Civ.
Eng . 97:617—628.
Kondo, R, K. Saineshim 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.
Kopperdahi, F.R. 1975. “Guidelines for Performing Static
Acute Toxicitiy Fish Bioassays in Municipal and Industrial
Wastewaters.” State of California. Fish and Wildlife
Water Pollution Control Laboratory.
Kruzynski, G.M. 1979. “Uptake and Distribution of Dehydro-
abietic Acid in Sockeye Salmon Smolts ( Oncorhynchus nerka )
and Mature Rainbow Trout ( Salmo airdneri ) .“ Unpublished
Paper, submitted to Journal of Fisheries Research Board of
Canada . l7pp + Figures.
Larson, G.L. and D.A. Schlesinger. 1978. “Toward an Understand-
ing of the Toxicity of Intermittent Exposures of Total Resi-
dual Chlorine to Freshwater Fishes.” IN: Water Chlorina-
tion: Environmental Impact and Health Effects . (R.J. Jolley,
H. Gorchev, and D.H. Hamilton, eds.). Ann Arbor Science
Vol I. pp. 111—122.
Leach, J.M. and A.N. Thakore. 1977. “Compounds Toxic to Fish
in Pulp Mill Waste Stream.” Prog. Wat. Tech . 9:787-798.
Lewis, B.G. 1966. “Chlorination and Mussel Control: I - The
Chemistry of Chlorinated Sea Water; A Review of the Lit-
erature.” Central Electricity Research Labs. l3pp.
Rock, Chet. May 24, 1978. Letter to J. F. Cormack, Crown
Zellerbach.
Rogstad, R.K. January 2, 1976. Letter to J.C. Knudson, DOE.
Olympia, Washington.
Rogstad, R.K. January 29, 1976. Letter to DOE, Olympia,
Washington.
Rogstad, R.K. December 30, 1976. Letter to Chet Rock, DOE.
Olympia, Washington.
Rogstad, R.K. January 3, 1977. Letter to Chet Rock, DOE.
Olympia, Washington.
Rogstad, R.K. July 13, 1977. Letter to Chet Rock, DOE.
Olympia, Washington.
Rogstad, R.K. July 12, 1978. Letter to DOE, Olympia, Washington.
250

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Rogstad, R.K. April 30, 1979. Letter to DOE, Olympia, Washington.
Rogstad, R.K. December 17, 1979. Letter to DOE, Olympia,
Washington.
Rosehart, R.G., G.W. Oxburn and R. Mettinen. June 1974.
“Origins of Toxicity inSuiphite Pulping.” Pulp and Paper
Magazine of Canada 75(6): 63—66.
Schink, T.D. and C.E. Woelke. 1973. Development of an in situ
Marine Bioassay with Clams . Final Report for Grant 18050DJ
to EPA, Environmental Research Laboratory, Naragannsett,
Rhode Island.
Seppovaara, 0. 1973. “The Toxicity of the Sulfate Pulp Bleaching
Effluents.” Paperi ja Puu . 55:713. (Ab. Bull. Inst. Paper
Chem. 44:10910).
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. “Measurement of Pollutant Toxicity to
Fish, III — Sublethal effects and ‘safe’ concentrations.”
Water Res . 5(6) :245—266.
Stein, J.E., R.E. Peterson, J.G. Denison, G.M. Clark and I.E.
Ellis. 1959. The Spawning of Olympic Oysters (Ostrea
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Research Division Report, Rayonier, Inc. Shelton, Washington.
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. Djnnel, E.F. Muriburt, and D.H. DiJulio. 1980.
“Acute Toxicity and Behavioral Responses of Coho Salmon
(Oncorhynchus kisutch) and Shiner Perch (Cymatogaster ag-
gregata) to Chlorine in Heated Sea-water.” Water Res .
14:347—354.
Sugam, R. and G.R. Helz. 1977. The Chemistry of Chlorine in
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Thatcher, T., J. Bridge and D. Wood. 1976. “Relative Sensitivity
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of Biomedical and Environmental Research, BNWL—2000, PT-2,
Battelle Pacific Northwest Laboratory, Richland, Washington.
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Thatcher, T.O. 1978. “The Relative Sensitivity of Pacific
Northwest Fishes and Invertebrates to Chlorinated Seawater.”
IN: Water Chlorination: Environmental Impact and Health
Effects . (R.L. Jolley, H Gorchev, and D.H. Hamilton, eds.).
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United States Department of the Interior Enforcement Project.
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in_Pu9 et_Sound.__U._S. Department of the Interior, Portland,
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Walden, C.C. 1976. “Review Paper: The Toxicity of Pulp and
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Walden, C.C. and D.J. McLeay. 1974. Interrelationships of
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CPAR ReportNo. 165-1. Canadian Forestry. Ottawa, Ontario.
Walden, C.C., D.J. McLeay and D.D. Monteith. 1975. “Comparing
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Watkins, S.H. June 7, 1977. Letter to J.F. McCormack, Crown
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Williams, R.W., W.E. Eldridge, E.M. Mains, A. Reid. 1953. A
Preliminary Report of an Investigation of the Toxic Eff cts
of Sulfite Pulp MiilWaste Liquor on Downstream Salmon
Migrants in Brackish Water . Washington State Water Pollution
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Wilson, M.A. 1975. Assessment of the Sensitivity of Major
Aquatic Food Chain Organisms to Newsprint Mi ii rtiuents
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Wilson, M.A. and C.I. Chappell. 1973. Reduction of Toxicity
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Wilson, R.C.H. 1972. “Acute Toxicity of Spent Sulphite Liquor
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Woelke, C.E. 1960a. “Effects of Sulfite Waste Liquor on the
Normal Development of Pacific Oyster ( Crassostrea gigasj
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Woelke, C.E. 1960b. “The Effects of Sulfite Waste Liquor on
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and Three of their Food Organisms.” Washington Department
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Woelke, C.E. 1960c. “Preliminary Report on Oyster Food
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Woelke, C.E. 1960d. “Preliminary Report of Laboratory Studies
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Woelke, C.E. 1965. Bioassays of Pulp Mill Wastes with Oysters.
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Woelke, C.E. 1972. Development of a Receiving Water Quality
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( Crassostrea 9i as) Embryp . Washington Department of
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Woelke, C.E. 1976. Measurement of Water Quality with the
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“Field Toxicity Studies and Juvenile Salmon Distribution in
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Control Federation 42(2):229—236.
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VI BIOLOGICAL RESOURCES
This chapter discusses the existing literature and data relating
to marine biological resources between the Elwha and the Dunge-
ness River along the Strait of Juan de Fuca (hereafter Strait)
shoreline. Much of the detailed information has been placed in
Appendices VI-A - VI-K and this section contains only summary
statements and tables. In order to key into the ecological dis-
cussion in Chapter VII, the organisms using the waters of Port
Angeles Harbor (hereafter Harbor), Strait and their tributary
streams are divided into the following groups:
A. Phytoplankton and other marine plants
B. Zooplankton
C. Shellfish
D. Other Invertebrates (crustaceans, benthos etc.)
E. Fish (marine and anadromous)
F. Wildlife (waterfowl and marine mammals)
Organisms within these groups form the major functioning portion
of the marine (and tributary stream) ecosystems. An inventory
of the major organism types occurring in Port Angeles Harbor and
the adjacent portions of the Strait are presented in Table VI—l.
The literature and data pertaining to these organisms is dis-
cussed in some detail in the sections below, since no previous
biological inventory has been completed for the study area.
Northern Tier Pipeline Company, however, has compiled a limited
inventory focused on Ediz Hook.
A. PHYTOPLANKTON AND OTHER MARINE PLANTS
This section is divided into subsections on 1) phytoplankton,
2) benthic and and macro algae, 3) seagrasses and 4) wetland
plants. All known marine related flora in the Port Angeles
area falls into one of these groupings. The subsections below
254

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Table VI-l. MAJOR ORGANIC GROUPS OCCURRING IN PORT ANGELES
HARBOR AND ADJACENT WATERS
Group Subgroup Number of Known Genera
Phytoplankton Green Algae Unknown
Blue-green algae Unknown
Eug].enoid Unknown
Diatoms 32
Dinoflagellates 2
Microflagellates Unknown
Zooplankton Ichthyoplankton 15 — 18
Other Zooplankton 23
Shellfish Hardshell Clams 5
Softshel]. Clams 5
Oyster (commercial) 1
Crustacean (commercial and
sport) 3
Other Marine
Invertebrates Benthic 181
Pelagic 24
Fish Anadromous 7
Marine 61
Marine Mammals Seals and Sea Lions 5
Dolphins, Porpoises, Whales 14
Other (Otter) 1
Marine Birds Loons 3
Grebes 4
Cormorants 3
Geese 4
Ducks 22
Gulls 7
Sandpipers 4
Other 12
255

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concentrate on abundance, biomass and seasonality of these
organisms. Diversity and productivity are discussed in Chapter
VII.
1. P ytop1ankton
Phytoplankton are typically the major primary producers of
energy in freshwater and marine ecosystems. They are free-
floating microscopic plants which change solar energy into food
for themselves and organisms higher in the food chain. Phyto-
plankton are distributed throughout the euphotic zone in the
Harbor and the Strait, although densities are variable, based
on physical dynamics of the water column and availability of
nutrients.
The majority of phytoplankton studies have been limited to
northern Puget Sound (San Juan Islands - see Phifer 1933,
1934) and Puget Sound proper. Published information of phyto-
plankton in Port Angeles Harbor is contained only in data from
2 stations at Ediz Hook sampled by the Northern Tier Pipeline
Company (NTPC 1979). The first major plankton survey of the
Strait occurred during a 20 month period beginning in February
1976 (Chester et a].. 1978). Phytoplankton groups found in the
study give a good context for conmiunities along the Strait of
Juan de Fuca. Six groups were identified:
• chiorophyta (miscellaneous green algae)
• cyanophyta (miscellaneous blue—green algae)
• euglenophyta (miscellaneous euglenoids)
• chrysophyta (coccolithophoridS, diatoms)
• pyrrophyta (dinoflagellates)
• miscellaneous microflagellates
In the Chester et a].. (1978) research, all phytoplankton samples
were collected from mid—channel stations; therefore species
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occupying nearshore or benthic habitats were not sampled.
As with most plankton studies, the results were
...complicated by both vertical and hori-
zontal patchiness and abrupt or slow seasonal
changes in addition to water circulation
patterns, grazing, circadian migration and
radiation fluctuation.
Three mid-channel stations (2,5, and 8) were sampled for
phytoplankton (Figure VI-1). Stations 1 and 2, approximately
four and ten miles offshore, respectively, are the locations
most representative of species occurring in the Port Angeles
vicinity. Samples were collected at 10 in intervals from
the surface to 50 m depth using 1.5 liter Niskin bottles.
Both chlorophyll a (for biomass determination) and species
abundance were determined from these samples.
There are roughly 120 - 150 known phytoplankton species present
in the study area (Appendix VI-A). The 35 dominant species in the
Strait as measured by Chester et al. (1978) are shown in Table
VI-2. Additionally Northern Tier Pipeline Company (NTPC 1979)
found Coscinodiscus, Fragilaria, Melosira distans and Thalas-
siusira nordenskoldii to be at least locally abundant at the
outer Harbor edge near Ediz Hook (Table VI-3). From Tables
VI-2 and VI-3, it appears that at certain times, miscellaneous
microflagellates may dominate the communities numerically. Due
to their greater size and density, however, centric diatoms
contribute the majority of phytoplankton biomass. Populations
of both diatoms and dinoflagellates were found to be highly
variable during the year. Diatoms tend to achieve maximum
concentrations during mid spring and early summer (Figure VI-2);
whereas dinoflagellates produced peak concentrations during
late summer and early fall (Figure VI-3).
Although they were present in insignificant quantities, the
populations of coccolithophorids are an important ecological
257

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Figure VI-1. AREA CHART AND STATION LOCATIONS FOR STRAIT
I OF JUAN DE FUCA CRUISES, FEB. 1976 - OCT. 1977
Source: Chester et al. 1978)
I
I

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Table VI-2. DOMINANT PHYTOPLANKTON SPECIES OF STRAIT OF
JUAN DE FUCA AT STATION 2
Source: Chester 1978.
Data collected at 0 m and 50 m depths
Group Abundance
Phylum/Class/Species (cells/liter)
1976 1977
Phylum Cyanophyta
Class Cyanophyceae
Misc. blue—green algae spp. 1202 3080
Phylum Euglenophyta
Misc. euglenoids 1214
Phylum Chrysophyta
Class Bacillariophyceae
Asterionella japonica 4815 2340
Asterionella spp. —- 6480
Chaetoceros affinis 133 7040
Chaetoceros brevis 6833 -—
Chaetoceros compressus 1647 17,020
Chaetoceros concavicornis 33 2940
Chaetoceros constrictus 324 9000
Chaetoceros debilis 14,632 4619
Chaetoceros decipiens 3885 2194
Chaetoceros didymus 3216 930
Chaetoceros radicans 6681 410
Chaetoceros similis 9211 990
Cy].indrotheca closterium 8440
Misc. Hyalochaete
chaetoceros spp. 34,270 4902
Melosira sulcata 18,168 14,580
Nitzschia delicatissima 1167 1149
Nitzschia longissima 2660 1145
Nitzschia seriata 300 3240
Rhizosolenia stolterfothii 342 2600
Skeletonema costatum 1,230,428 7178
Thalassionema nitzschiodes 6397 6636
Thalassiosira aestivalis 7212 4040
Thalassiosira condensata 3400 4770
Thalassiosira decipiens 2617 30
Thalassiosira nordenskioldii 16,950 66
Thalassiosira pacifica 838 1559
Thalassiosira polychorda 33 1850
Thalassiosira rotula 5260 9690
Misc. Thalassiosira spp. 15,580 2440
Misc. Pennate diatoms 85 1550
Phylum Pyrrophyta
Class Dinophyceae
Peridinium spp. 132 1107
Peridinium discoides 2350
Microflagellates
Misc. microflagellate spp. 487,225 200,652
259

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Table VI-3.
DOMINANT PHYTOPLANKTON DENSITIES IN THE VICINITY OF PORT ANGELES HARBOR
DURING FEBRUARY AND APRIL 1978
Source: Northern Tier Pipeline Company 1979
Taxa
Station 3
Upper
Lower
Upper
February I April r February I April
Depth Interval
Lower
Station 5
Upper
Lower
Upper
Lower
Coscinodiscus spp. *
Fragilaria sp.
Melosira distans*
Nitzschia longissima
Nitzschia spp.
Paralia sulcata*
Skeletonema costatum*
Thalas s ionema
nitzschioides
Thalassiosira decipiens*
Thalassiosira
nordenskoldi i *
Thalassiosira spp.*
Unidentified Centric
Diatoms
Unidentified Pennate
Diatoms
Total Mean Density
244**
P
302
P
1,450
P
P
p
404
P
P
3,290
P
P
532
P
4,220
P
P
1,420
585
P
518
9,800
P
P
P
P
P
29,400
14,600
8,500
P
6,760
P
99,500
P
P
P
P
P
28,900
10,500
P
3,770
P
P
P
63,500
P
1,030
P
1,040
5,140
P
P
1,230
2,320
2,330
980
18,300
P
1,500
P
P
P
5,330
P
P
1,460
1,840
1,700
P
16,300
P
P
P
P
P
P
26,700
3,220
3,180
3,580
3,220
P
P
59,600
P
P
P
P
P
17,700
3,960
3,180
P
3,300
p
P
43,200
*Centric diatoms
**Density is in units per
++p means present but not
liter.
as a dominant.

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-J
t ) -
0
1 3
0
5
4.
3-
S Station 2
I I I I I I I I
I I I I I I I I I -— I I
I I I
J F M A M .1 J A S 0 N D J F M A N J J A $ 0 N D
1976/1977
Figure VI-2. DIATOM CONCENTRATIONS IN THE UPPER 1 METER, STRAIT OF JUAN DE FUCA
ADJACENT TO PORT ANGELES HARBOR.
Source: Chester et al. 1978

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4
3
3
3
! 2
I
0
1
— I i I I I I I I I . a I I I I I I I
J F N A N J J A $ 0 N D J F N A N J J A $ 0 N 0
1978/1977
Figure VI-3. DINOFLAGELLATE CONCENTRATIONS IN THE UPPER 1 METER, STRAIT OF
JUAN DE FUCA ADJACENT TO PORT ANGELES HARBOR
•Statlon 2
Source: Chester et al. 1978

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indicator. This species occupies Washington coastal areas;
however, these organisms are not known to be typical of
Puget Sound. The presence of coccolithophorids in the Strait
probably results from the transport of oceanic populations.
This indicates the presence of a transitional marine community
near Port Angeles.
2. Benthic and Macro—algae
In addition to phytoplankton, benthic diatoms and various
macrophytic algae are found near Port Angeles. Benthic
diatoms exist in and on bottom sediments; however, data on
species present, densities or productivity are essentially
nonexistant. It is probable that some of the planktonic
genera may form benthic colonies in the shallow nearshore
zones; however, it is not known whether there are other benthic
types which are not represented in the plankton.
Macro-algae are macroscopic algae which are generally attached
to the substrate except when broken off by wind or wave aqtion.
In the Port Angeles area, these are known to include such
shallow intertidal types as sea lettuce ( Ulva spp.) and bladder
kelp ( Fucus spp.) as well as the deeper water laminarian keips
( Nereocystis spp).
No comprehensively detailed distribution studies exist on
macro-algae in Strait Juan de Fuca although DOE has mapped
portions of the shoreline in a general sense (Figure VI—4).
Over 50 species of macro-algae were found at Neah Bay (Rigg and
Miller 1949) in rock habitats. Most of these were red and
brown algae. It is doubtful, although possible, that this
diversity exists at Port Angeles. Most of the algae at Neah
Bay were red and brown varieties which are probably restricted
to oceanic waters and which are not found in the inner reaches
of the Strait or Puget Sound (Gardner 1978). Northern Tier
reports mainly red and brown macro—algae at the mouth of
263

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12f2$
12 t28 12 r21 123126
Strait ol Juan de Fuca
12f25 12i24 1Zf23 12t22 12i21 123’20
o !
Figure VI-4. DISTRIBUTION
OF CONCENTRATED MACRO-ALGAE AND SEAGRASS
L
BEDS NEAR
PORT ANGELES
Source:
DOE
1978
4Voe’
48’oe’
A
A
Port Angeles Harbor
48’04
A — S..grsss
B - Community
C — Othw Algal Community
4V06
4VO

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Morse Creek as the major portion of the 30 species found
(Table VI-4). Field observations in the area by NEC staff
also showed the large kelp Nereocystis to be found off the
outside of Ediz Hook and in occasional other locations on the
shoreline.
3. Seagrasses
Seagrasses are marine seed bearing plants (angiosperms)
which are similar to terrestrial grasses in general appearance.
In the Port Angeles area eelgrass ( Zostera marina ) is the only
species of note. Eelgrass provides habitat for critical life-
stages of fish and certain invertebrates. Eelgrass is also a
prime food source for waterfowl (see Section VI.F). Figure
VI—4 shows known eelgrass beds near Port Angeles. There are
also significant eelgrass beds east of Port Angeles on the
inside of Dungeness Spit (DOE 1978). The growth pattern and
light requirements of seagrasses restrict them to the shallow
near surface zone, where they tend to be exposed to low density
effluents such as spent sulfite liquor (SSL).
4. Wetland Plants
Due to the high energy environment along most of the shoreline
of the Strait, marshes are rather small and restricted to
limited areas. A very small high marsh at the mouth of Morse
Creek supports various grasses and sedges however, the closest
large marsh east of Port Angeles occurs on the inside edge of
Dungeness Spit. This area is currently protected as a National
Wildlife Refuge by the U.S. Fish and Wildlife Service. The
marsh is dominated by pickleweed ( Salicornia virginia ) and
saltgrass ( Disticlis spicata ) with lesser amounts of other
marine grasses and sedges. A list of plants found by Northern
Tier Pipeline Company is shown in Appendix VI-B, Table VI-B-1.
265

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Table VI-4. MACRO-ALGAE AND SELECTED EPIPHYTES FROM THE LOWER
INTERTIDAL ZONE AT MORSE CREEK, APRIL 1978
Source: NTPC 1979
Taxon Dominance Classification
DIVISION RHODOPHYTA (Red Algae)
Ahnfeltia plicata
Callophyllis fabellulata
Cryptonemia borealis
Delisseria decipiens
Erythrophylluxfl delesserioides
Gigartina papillata W, N
Iridaea cordata W, N
I. heterocarpa N
mbranoptera sp.
Odontha].ia floccosa
0. washingtoniens is
Polyneura latissima
Polysiphona sp.
Porphyra miniata
P. schizophylla N
iφnitis lyallii
Ptilota filicina
Rhodymenia pa].mata W, N
Schizyinenia pacifica
Unidentified Red Algae
DIVISION PHAZOPHYTA (Brown Algae)
Alaria marginata W, N
Cymathere triplicata W
Desmarestia kurilensis
D. ligulata
Ectocarpus parvus
Lantinaria dentigera W
L. saccharina W
L sinclairii
Pterygophora californica
Unidentified Brown Algae
DIVISION CHLOROPHYTA (Green Algae)
Cladophora stimpsonii
Enteromorpha intestinalis
* g fljS flS considered dominant by weight constitute greater than or
equal to 2.00% of the total wet weight.
**Orgaflislfls considered dominant by number constitute greater than or
equal to 2.00% of the total number.
266

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B. ZOOPLANKTON
Zooplankton in the Puget Sound waters comprise one of the
more important components of the marine ecosystem due to their
substantial biomass and their position in the food chain.
Zooplankton (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 commercially
valuable fish in the Strait, as well as the Puget Sound Basin.
Zooplankton can be divided into three main categories which
are:
• Ichthyoplankton,
• Microzooplankton,
• Mac rozooplankton.
Icthyoplankton include the eggs and larval forms of fish and
shellfish, many of which are commercially important in their
adult stages. Microzooplankton are mainly protozoan or
metazoan organisms of microscopic size. Other zooplankton are
generally classified as macrozooplankton which include a large
number of minute, but visible marine animals.
The vertical and horizontal distributions of zooplankton in
the marine waters are dependent upon several factors. These
include season, location, illumination, time, and hydrographic
conditions, as well as physical factors. The zooplankton com-
munity in the Strait consists of several hundred oceanic species.
The number of oceanic species in the Strait decreases from west
to east, being replaced by estuarine species better adapted to
the conditions of the Puget Sound Basin.
Studies on the zooplankton found in the Strait are extremely
limited. Known research pertinent to Port Angeles includes
only a two year study conducted by the Pacific Marine Environ-
mental Laboratory between 1976 and 1978 (Chester et al. 1978),
267

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and two monthly samplings at two stations in Port Angeles
by Northern Tier Pipeline Company (NTPC 1979).
Chester et al. (1978) sampled zooplankton periodically at
the 9 stations described under phytoplankton above (see
Figure VI-l). Methods included oblique tows, pleuston tows
and vertical hauls. Stations 1 and 2 are nearest the Harbor
and best represent the planktonic fauna at Port Angeles.
Chester and co—workers found that zooplankton in the Strait
were a mixture of cold temperature species and warm transi-
tional species. The data indicate that zooplankton were least
abundant during fall/winter (September - March) and most abun-
dant during spring/summer (April - August). The most numerous
types were oligotrichs (60%), gyrianostone (30%) and tintinnid
(10%) species (Chester et al. 1978).
Northern Tier Pipeline Company collected samples during Feb-
ruary and April of 1978. One station (#3) was located 0.5
miles west of Morse Creek (east of the ITT Rayonier diffuser),
while the other (#5) was located in Port Angeles Harbor itself.
Sampling was conducted using oblique tows with a plankton net,
sized to gather primarily macroplankton and ichthyoplankton.
The Northern Tier studies also found large seasonal fluctuations
with values ranging from 182 - 2257 individuals per cubic meter
representing the February — April values, respectively, in the
Harbor. Near Morse Creek the values were more extreme with 94 —
2600 per cubic meter representing February and April measurements.
1. Ichthyoplankton
There are many nonplankton marine organisms which do pass
through a planktonic stage (i.e. eggs and larvae). Chester et
al. (1978) calculated the number of eggs and larvae present in
the Strait at 1.3 billion and 30 billion, respectively, to a
depth of 50 meters. Selected abundances at stations offshore
from Port Angeles are shown in Table VI-5
268

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Table VI-5. ICHTHYOPLANKTON SPECIES FOUND IN THE WATERS ADJACENT
TO PORT ANGELES HARBOR AT STATIONS 1 AND 2
Source: Chester et al. 1978
GROUP
Abundance/rn 3
Family/Species Location 1976
1977
ICHTHYOPLANKTON LARVAE
Anunodytidae 2 35
AlTunodytes hexapterus 1 12-100
2 738
Clupeidae
Clupea harengus pallassi 1 4
Cottidae 1 16—111
2 51
Clinidae
Gibbonsia spp. 1 -- 177
Cyc lopteridae 1 4
2 3
Osrneridae 1 69—100
Gadidae 1 4—177
2 985
Microgadus proximus 1 203
Pleuronectidae
Parophrys vetulus 2 3
Scorpaeriidae
Sebastes spp. 1 15
Stichaeidae 1 15
2 6
Zanio lepidae
Zaniolepis latipinnis 1 69
Unidentified Ova 2 3
ICHTHYOPLANKTON FISH OVA
Pleuronichthys decurrens* 1 10—17
2 69
p. coenosus* 2
* Indicates data which were obtained using a pleuston tow and are
given in nuxnber of organisms/tow.
All other data are from oblique tows and are given in number/rn 3 .
269

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During the late winter and spring, the most common larvae
collected by oblique tow in the top 50 m of the
Strait were smelt ( Osxneridae ) and cod ( Gadidae) . The smelt,
cod and sandlance families seemed to show no preference for
surface water. Cod, in particular, were considerably more
abundant in the central Strait than at Station #1, which is
only four miles off Port Angeles. These abundances, however,
fluctuate considerably due to fish schooling and other factors
which create patchy distributions.
Northern Tier (NTPC 1979) sampled ichthyoplankton at 7 stations
(Figure VI-5) between the Elwha River and Dungeness in the spring
of 1978. Data from these samplings are contained in Appendix VI-C.
These data show sandlances still a dominant species; however,
the cod and smelt have been largely replaced by herring, rock-
fish, gunnels, prickleback and sculpins, most of which tend to
prefer nearshore habitats.
2. Nicrozooplankton
The protozoan and metazoan microzoop].ankton found in the Strait
represent a small portion of the total biomass of zooplankton;
however, they often form key links in the food chain or decom-
position process of ecosystems (Nixon, personal communication
September 19801. Chester et al. (1978) found that ciliates
were the most numerous xuicrozooplanktori in the Strait,
oligotrichs, tintinnids and active phytoplankton grazers were
the most common ciliates found.
Non—ciliated microzooplankton included dinoflagellates (see Section
VI.A), foraminiferans, radiolarians, juvenile crustaceans, and
trochophore larvae. However, these organisms were seen only
occasionally, whereas rotifers were frequently seen. All of
the microzooplankton species exhibited the same general pattern in
regard to abundance. The maximum microzooplankton abundance
parallels that of the dinoflagellate phytoplanktofl , reaching
their peak in mid to late summer.
270

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Prot.ction
L .
:
0 •
.-
4.
Numbsrs ndicat• IchthyopIankton
Sampling Stations
STRAIT OF JUAN DE FUCA
Crown
Z. II.rbach
lB
Figure VI-5. ICHTHYOPLANKTON STATIONS SAMPLED BY NORTHERN TIER PIPELINE CO.
Source: NTPC 1979

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3. Macrozooplaflktofl
Chester et al. (1978) divided the large zooplankton into six
categories. These are 1) oceanic copepods occurring below 50m,
2) oceanic copepods occurring at the surface occasion-
ally 3) oceanic surface - living copepods, 4) euphausids,
5) chaetognaths, and 6) amphipods. Those species represented
by the above classes are listed in Table VI-6.
The copepods occurring below 50 meters were the most abundant
zooplankton in the deeper samples. They were also most common
at the western stations due to the shallow area at Admiralty
Inlet which prevented their movement to the east. Copepods in
category 2 were normally found at depths below 50 m; however,
they occasionally occurred at the surface and have been found
in Puget Sound and Hood Canal. A third group of copepods which
are characterized as oceanic surface — living were also found
to occur occasionally in the Strait.
Overall, the most abundant zooplankton found by Chester et al.
(1978) were the copepods, which were represented by approxi-
mately 60 species. The most abundant copepods found in the
Strait are members of the genera Pseudocalanus, Acartia and
Oithona (Chester et al. 1978). Calanus marshallae which is
one of the more important zooplankton grazers in the Strait,
is very abundant during the spring and summer, but is completely
absent during the fall and winter (Frost 1974).
Euphausids (small shrimplike crustaceans) are also common in
the Strait; however, they are not as abundant as the copepods.
According to Parson and LeBrasseur (1970), the euphausids are
important filter feeding pleopods which link the lower trophic
levels to the larger carnivores (fish and whales). Chester
al. (1978) found five euphausid species of the genera
272

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Table VI-6. ZOOPLANKTON SPECIES FOUND IN THE WATERS ADJACENT
TO PORT ANGELES HARBOR AT STATION 2.
Source: Chester et a].. (1978)
Abundance/rn 3
Group 1976 1977
Subclass Copepoda
Order Calanoida
Acartia c].ausii 12 1
A. longiremis 130 357
Aetideus armatus 0 1
Calanus pacificus 3 6
C. plumchrus 4 1
C. marsha] .lae 200 80
Centrorhynchus abdominalis 7 4
Copepoda nauplii 139 113
pila longipedata 18 6
Eucalanusbungii bungii 0 2
Heter. longicornis 0 1
Metridia lucens 32 56
Microca].anus spp. 50 37
Paracalanus spp. 73 12
Pseudocalanus spp. 5769 3976
Racov. antarticus 0 1
Sco].ecithri. minor 5 2
pino. longicarnis 0 1
Torta. discaudatus 78 60
Order Cyclopoida
Corycaeus ang].icus 4 33
Oithona similis 250 427
0. spinirostris 31 5
Oncaea borealis 11 5
0. p o1ata 15 6
Pseudolupodia dilatata 8 2
273

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Table VI—6 continued
3
Abundance/rn
Group 1976 1977
Order Amphipoda
Parathemisto pacifica
Hyperia rnedusaruxn
17
0
8
5
Phylum Chaetognatha
Sagitta elegans
59
52
274

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Euphausia and Thysandessa inhabiting the Strait. Euphausids
were found to be most abundant during late spring and early
summer. Sampling counts at Station 2 were 41/rn 3 in the upper
25 m (May 1976) and 123/rn 3 in the 50 to 100 m depth
(June 1977)
Other zooplankton which are frequently found in the Strait
include the arrowworms ( Chaetognaths) . There are four species
of arrowworms found in the Strait, of the genera Sagitta and
Eukrohnia. Sagitta elegans was the most abundant chaetognath
found with densities greater than 100/rn 3 . This species is
usually a carnivore, feeding on copepods, or a detritus feeder.
The last group of zooplankton found in the region included
several different species of amphipods. These organisms are
generally scavengers feeding on detritus and are represented
by eight families in the Strait. The amphipod Parathemisto
pacifica was the most abundant (25 to 50/rn 3 ) organism in the
fall of both 1976 and 1977.
Northern Tier (NTPC 1979) studies agreed with Chester et al.
(1978) data that the most abundant zooplankton were calanoid
copepods, usually found in near surface waters. Densities of
these organisms ranged from 100 — 600 individuals per cubic
meter, at nearshore sampling locations (Figure VI—6). These
levels are considerably higher than those of other zooplankton.
These organisms were therefore found to comprise a vital link
in the trophic structure, possibly supplying a majority of the
bioinass transfer between plants and animals. The euphausids
were also found to comprise an important link in the food chain.
Although their densities are lower, they are preyed on directly
by many larger carnivores (Parson and LeBrasseur l97Q).., resu1t
ing in a highly efficient transfer from plants to the top
levels of the food chain. Other abundant non-copepod taxa
in the Port Angeles area stations were found to be barnacle
nauplii (in early stage), calanoid copepodites, adult copepods
275

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Figure VI-6. ZOOPLANKTON
STATIONS SAMPLED BY NORTHERN TIER PIPELINE CO,
Source: NTPC 1979

-------
( Calanus marshallae, Centropages abdominalis and Pseudocalanus
spp.) and tunicates ( Oikopleura doica) . Densities were gener-
ally found to be within the range of those reported by Chester
et al. (1978); however no specific comparative analysis appears
to have been carried out. Oithona similis was found to be sig-
nificantly lower in density at Port Angeles. It should be
noted that although copepods and other zooplankton are among
the most important ecological link, almost no information
exists as to the effects of pulpmill effluents on these organ-
isms.
Recently, Sirnenstad et a].. (1980) recorded 235 taxa of epi-
benthic invertebrates which included some species considered
to be macrozooplankton. He found that at shallow sublittoral
sites, harpacticoid copepods contributed over 75% of the total
biomass. They found that sandy substrates with heavy eelgrass
beds had the largest diversity and biomass. It was also noted
that gaminarid amphipods often contributed to a large fraction
of the living biomass and are important prey organisms for
many nearshore fishes and shorebirds.
C. SHELLFISH
Generally shellfish are aquatic invertebrates possessing an
external shell covering. The Washington State Department of
Fisheries (WDF) defines shellfish as invertebrate fish. As
filter feeders,shellfish concentrate trace substances including
pollutants and toxic contaminants present in their surrounding
water. Due to their very nature as filter feeders, shellfish
are subject to bioaccumulation of toxic substances which may
pose a threat to human consumers.
During the past eleven years (1969 - 1980) the WOF and DOE
have conducted shellfish surveys revealing 20 species in the
277

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Port Angeles — Dungeness area (Table VI-7, VI-8). Each of
these surveys was specific for commercial and/or non—commer-
cial clam species, Pacific oyster or Dungeness crab. All the
hardshell clam species listed in Table VI—8 and the Dungeness
crab are important commercial and sport harvested species.
The Pacific oyster located in Dungeness Bay is strictly for com-
mercial harvest. The Eastern soft shell and jackknife clams are
considered to be a sport harvested species in Washington waters
(Goodwin 1973a; WDF 1976). The remaining soft shell clams and
the tel].en are not usually utilized commercially or for sport
in Puget Sound (Goodwin 1973). Even though shellfish surveys
provided data on only 20 species, other invertebrate studies
reveal additional shellfish species in the study area (refer
to section VI.D.).
1. Shellfish Survey Methods
From 1967 — 1978 subtidal clam surveys were conducted in the
study area on various occasions. During January and February
1969 a survey to evaluate clam stocks in the Harbor was conduct-
ed by WDF in cooperation with the Washington State Water Pollu-
tion Control Commission (WPCC) (Goodwin and Westley 1970). The
water depth in the southern portion of , the Harbor is 60 ft (18.3 m)
or less compared to the 192 ft (58.5 m) depths in the northern
area. Due to the survey methodology (scuba and eductor dredge)
that limited work to 80 ft (24.4 m) depths and the required
clam substrates of sand, gravel, shell or mixtures of these,
the survey was confined to 48 stations in the southern portion
of the Harbor where those conditions prevailed.
An eductor dredge was used by scuba divers to sample areas
2 ft 2 (18.6 m 2 ) to a depth of 18 inches. The dredged
material was passed though a 1 inch mesh collection basket.
Both commercial. and non—commercial species of live clams,
dead clams and broken clam shells were collected and identified.
278

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Table VI—7. SUMMARY OF SHELLFISH SURVEYS IN THE PORT ANGELES - DUNGENESS AREA
Date Location Subject Objective Source
1967—1978(a) Port Angeles - subtidal hardshell clams assessment of commercially Goodwin 1973;
Dungeness area leasable shellfish beds Goodwin and Shaul
1978; Goodwin and
Shaul 1978(a)
1967-1978(a) Port Angeles - geoduck clams assessment of commercially Goodwin 1973a;
Dungeness area leasable geoduck beds Goodwin 1978; Good-
win and Shaul 1978b
January & Port Angeles Harbor subtidal hardshell clams determine distribution and Goodwin and Westley
February abundance of clams in Harbor 1970
1969 (b) area; conducted in conjunc-
tion with other pulp mill
effect studies
July 1969 Port Angeles Harbor intertidal clams provision of baseline data Bishop and Devitt
to document conditions prior 1970
to anticipated pulp mill ef f-
luent treatment methods
April 1975 Port Angeles Harbor intertidal clams follow-up of July 1969 study; Kittle 1976
provide baseline data in anti-
cipation of oil terminal loca-
tion in area
1975-1978 Port Angeles - crab and shrimp determine location and magni- Bumgarner 1977;
Dungeness area tude of commercial and recrea— Bumgarner 1979
tional crab and shrimp fishery
unknown Dungeness Bay Pacific oyster locate commercial oyster beds DNR 1977
(a) Surveys were not conducted solely in the Port Angeles - Dungeness area throughout this time
period.
(b) Data collected during January and February 1969 for commercial clam species were incorporated
in Goodwin 1973.

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Table VI-9. COMMERCIAL AND NON-COMMERCIAL SHELLFISH
SPECIES SURVEYED IN PORT ANGELES, WASHINGTON
PHYLUM MOLLUSCA
Class Pelecypoda
Hardshel]. clams
Butter - Saxidomus gigantena
Cockle - Clinoaardiurn nuttali
Geoduck — Panope gerierosa
Horse — Tresus capax
Tresus app.
Native Littleneck - Protothaca atarninea
Softshell clams
Bent—nose — Macoma nasuta
Macoma — Macama app.
Polluted macoma — Macoma irus
Eastern softshell — Mya arenaria
Truncate softshell - Mya truncata
Miscellaneous clams
Blunt jackknife — Solen sicarius
Milky Pacific venus — Camp somyax aubdiaphana
Panomya ampla
Tellen - Tellina app.
Qys ters
Pacific oyster — Crassostrea gigas
PHYLUM ARTHROPODA
Class Crustacea
Crabs
Dungeness crab - Cancer magia tar
Shrimp
Coon shrimp - Panda lus danae
Pink shrimp - Panda lus jordani
Pandalus borealis
280

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Beginning in 1967 the WDF initiated surveys on commercial
hardshell clam stocks in Puget Sound (Goodwin 1973). The
overall purposes of the surveys were to 1) survey subtidal
hardshell clams in the state, 2) assess their potential for
commercial harvest and commercially leasable sites and 3)
develop long range management policies for subtidal clams
(Goodwin 1973; Goodwin and Shaul 1978; Goodwin and Shaul
1978a). The data collected on butter and littleneck clams
in the 1969 study was subsequently incorporated into the
report summarizing the subtidal hardshell surveys conducted
from 1967 — 1971 (Goodwin 1973).
The WDF sampled locations in water depths ranging from 4-70 ft
(1.22-21.3 m) , based on 0 tidal level, according to the “grid”
or “spot check” method (Goodwin 1973). In unexplored areas
sample sites were established in a regular fashion; however
intensity varied with each site. The larger the area the lower
the intensity (one sample per 100 or 200 acres). The areas
where clams were known to exist were marked with buoys (grid
method). Evenly spaced transect lines were established and
samples were taken along the lines of equal intervals. This
allowed for a higher sample intensity than the spot check
method.
Samples (2 ft 2 (18.6 cm 2 ) each) were collected with a
hand held venturi dredge. The vacuum material passed through
a 1 inch (2.5 m) mesh basket. Despite the fact the study was
specific for hardshell clam species, all collected clam species
were identified. Only the data on butter, littleneck and
occasionally horse clam species collected in the sampled areas
were provided in the reports.
During the subtida]. hardshell clam surveys (1967 - 1978) geo—
ducks, located in the subtidal waters were also surveyed (Good-
win 1973a; Goodwin 1978; Goodwin and Shaul l978b). Despite
the fact the geoduck is a hardshell clam, the location of these
clams in the substrate requires a different survey method than that
281

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Used for the other subtidal clams (venturi dredge). The
geoduck surveys were conducted along 150 ft (45.7 m) tran-
sects that were 6 ft (1.85 m) wide. These transects ran
perpendicular to shore from 30 ft depths out to 50 or 60 ft
(15.2 - 18.3 in) depths. Divers counted the geoduck si-
2 2
phons or their marks located in the 900 ft (83.6 m ) area.
These visual counts were adjusted with a monthly “show” factor
to provide a more accurate total for each transect (Goodwin 1978).
Since 1969 DOE has conducted two intertidal (1.6’ to 00’ tidal
level) surveys of both commercial and non-commercial species
occurring in the Harbor (Bishop and Devitt 1970; Kittle 1976).
The first study, initiated by DOE’S predecessor, the WPCC, in
July 1969, was conducted to document 1969 baseline intertidal
clam populations for future evaluation of anticipated modi-
fications to pulp mill effluent treatment and discharge methods
(Bishop and Devitt 1970). The second study, which duplicated
the methods and transect locations of the first, was conducted
in April 1975 to provide new data for oil pollution baseline
studies in anticipation of a possible oil terminal port faci-
lity at Port Angeles (Kittle 1976).
During low tide three beaches in the Harbor were sampled every
400 ft (121.9 m) along the tideline. Each sample consisted
of a 2 ft 2 (18.6 cm 2 ) surface area dug to a depth of 0.5 —
2.0 ft (.15 — .61 in). The sample was screened through 0.5
inch (1.27 cm) mesh to retrieve the intertidal clams.
According to the Washington Department of Natural Resources
(DNR 1977), Pacific oyster culture beds are located in Dunge-
ness Bay. The DNR report utilized existing information to
plot the oyster bed locations but the specific source and data
utilized is not provided (Figure VI-7).
Unlike the sample surveys conducted on subtidal and intertidal
clams, data on the Dungeness crab and shrimp was compiled from
282

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commercial and sport data retrived from fishermen and/or
fish receiving tickets by the WDF (Bunigarner 1977, 1979).
2. Shellfish Survey Results
Subtidal Ciams: During the 1969 survey (Goodwin and Westley
1970), several commercial and non—commercial clam species were
retrieved. The authors concluded that subtidal populations
of commercially important clams (butter, littleneck, and horse
clams) historically existed in the Harbor and continue to do
so. No comparisons of 1969 populations with historical popu-
lations were made. It is unlikely that any quantitative com-
parison could be made due to an apparent lack of pre-1969 data.
The greatest concentrations of clams occurred in coarse sedi-
ments, the least dense concentrations occurred in fine grain
sediments and areas containing pulp mill sludge. Both commer-
cial and non-commercial species were most abundant on a shelf
east of ITT Rayonier (Appendix VI-D , Figures VI-D-l and VI-D-2).
No live clams were found in areas where sludge was two inches
or greater in thickness.
Based on the presence and depth of shell deposits, Goodwin
and Westley speculated that clams had been present in the
Harbor for a considerable time, perhaps thousands of years,
and that no substantial change in species composition had
occurred. The high percentage of hinged shells (recent deposits)
(47%) west of ITT Rayonier with those east of the mill (37%)
suggests mortalities were higher west of the mill. This was
further supported by the low numbers of live clams sampled
west of the mill even though large shell bed deposits (both
hinged and fragments) existed in the area (Figures VI-D-1,
VI-D—2, VZ—D-3).
The most recent survey of commercial subtidal hardshell clam
beds in the Port Angeles area was conducted by the WDF sometime
283

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between 1973 and 1977 (Goodwin and Shaul 1978). The results
identified subtidal clam beds for butter, littleneck and horse
clams are in Port Angeles Harbor, Green Point, Dungeness Spit
and Dungeness (Figure VI-7). The acreage, estimated number of
pounds of each clam species and the density of clams for each
bed is summarized in Table Vi-9. In addition to major clam
beds, the WDF also identified locations in which at least one
market sized littleneck or butter clam was sampled. For addi-
tional data on each sample taken in the Port Angeles - Dungeness
area, including the substrate type and cover, refer to Appendix
vI-D.
A review of each sample site’s substrate composition shows all
of the clam beds occur in areas east of ITT Rayonier that are
free of sludge and wood debris (Table VI-D-l). Only two Harbor
sample sites containing sludge in their bottom substrate were
found to contain clams (Stations 15 and 46). Due to the present
treatment facilities the ITT Rayonier mill is no longer dis-
charging significant quantities of sludge to receiving waters.
In 1975 a SCUBA inspection of ITT Rayonier’s sludge beds im-
mediately east and west of the mill showed a thin layer of
sludge covering an underlayer of sand that also contains some
sludge (Moore 1976). These beds are affected by tidal and wave
action which is slowly dissipating the beds and their toxic
condition (Moore 1976).
Geoduck: Initially the geoduck was an important sport fishery,
but in 1969 the species was designated as both a sport and com-
mercial species. Regulations of the commercial geoduck fishery
are required in order to obtain the management resource goal
(to sustain a permanent yield) (Cumbow 1978). Commercial har-
vesting of geoducks is prohibited in beds within Ό mile seaward
of the mean high water line or in waters shallower than 10 feet
(3.05 m) below mean lower low water. Due to these restrictions
all subtidal harvest is located on public land managed and
leased by the Department of Natural Resources (subtidal bottoms
284

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I Ppotsctlon
-.*
0
0 .
.-I
Figure VI-7. LOCATIONS OF MAJOR HARDSHELL CLAM, GEODUCK CLAM AND PACIFIC
OYSTER BEDS IN THE PORT ANGELES - DUNGENESS AREA
Source: Goodwin 1978; Goodwin and Shaul 1978;
Goodwin and Shaul 1978b; DNR 1977
12?30’ 12t20’
- G.oduck
Clams
- “ ‘ ‘ STRAIT OF JUAN DE FUCA
uaw; Clams
ri-n —
LIJJ Oyst.t
12 II 101
miles

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Table VI-9. ESTIMATED CLAM POPULATION AND DENSITY OF MAJOR BEDS IN THE PORT ANGELES AREA
Source: Goodwin and Shaul 1978a
Location
Acreage
lbs of Clam Species
Density
lbs/acre
Butter
Littleneck
Horse
Port Angeles
100
1,566,592
1,000,878
913,845
34,813
(Figure VI-D—5)
Green Point
467
10,171,260
10,171,260
1,830,827
29,185
(Figure VI-D-6)
Dungeness Spit
356
13,162,743
2,477,693
3,251,972
53,069
(Figure VI—D—7)
Dungeness
20
270,072
174,240
740,520
159,242
(Figure VI—D—8)

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below the lowest tide level in Puget Sound, approximately -4.5
ft (-1.37 m) level (Goodwin l973a).
Commercial harvesting is restricted to divers using hand-held
manually operated equipment. The economically maximum depth of
harvest is usually 60 feet (18.3 m); however, geoducks occur
between tidal elevation -2.0 feet (.61 m) to depths of 155 feet
(47.2 m) or more (Goodwin 1973a).
The WDF (Goodwin 1978; Goodwin and Shau]. l978b) defined three
major geoduck beds in the Port Angeles — Dungeness area (Figure
VI-7, Appendix E, Figures VI-E-1, VI-E-3, VI-E—4). The estimated
population of each bed is shown in Table VI—lO. In addition
to these beds geoducks were also found in two separate locations
between Angeles Point and the base of Ediz Hook (Figure VI-E-2).
These two beds totaled 238 acres and supported an estimated
population of 426,000 geoducks (Goodwin 1973a). Geoduck tran-
sect counts, water depth and substrate information are provided
in Table VI—E-l.
No geoduck surveys were conducted along outer Ediz Hook because
the 60 foot (18.3 m) contour falls inside the Ό mile offshore
limit. No surveys were conducted inside Port Angeles, nor were
surveys conducted east along the Straits between Port Angeles
and the mouth of Morse Creek. The absence of geoducks off the
mouth of Morse Creek (Stations 1 and 2, Figure VI-D-3) can be
explained by bottom characteristics. Substrate particle size
here ranges from pea gravel to boulders. Nowhere in the vicinity
does this type of substrate support geoducks.
According to the most recent survey of geoduck beds in the
study area (Goodwin and Shaul 1978b) both the Green Point and
Dungeness beds contain leasable areas. These areas must meet
state laws and regulations with respect to commercial geoduck
fishing to be considered a leasable bed. At one time, 1,000
287

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Table VI-].0. ESTIMATED GEODUCK POPULATION AND DENSITY
OF MAJOR BEDS IN THE PORT ANGELES AREA
Source: Goodwin 1978
Density
Location
Acreage
Population
clams/acre
Green Point
1,935
6,583,876
3,403
(Figure VI-E-3)
Nos. 3,6—14,17
Green Point
1,582
4,310,823
2,725
(Figure VI-E—3)
Nos. 21,22,24—27,29
Dungeness Bay
1,895
7,089,801
3,741
(Figure VI—E—4)
288

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acres (4.05 x 107 m 2 ) of Green Point beds were considered to
be commercially leasable (Goodwin 1973a). Subsequently this
estimate has been revised (Goodwin and Shaul 1978; Goodwin and
Shau]. 1978b) to cover only 600 acres (2.43 x 106 m 2 ) which are
estimated to contain 3,479,000 geoducks. This is the largest
unleased commercial geoduck bed in the State of Washington.
As of 1978, 120 acres (4.86 x 105 m 2 ) of the Dunge—
ness Bay bed was under lease while 430 acres ( 1.74 x 106 m 2 )
containing an estimated 2,171,000 geoducks remained available
for commercial lease (Goodwin and Shaul 1978b).
Available information demonstrates the presence of commercially
valuable geoduck resources in an area peripherally affected by
pulpmill effluents. - A summary of geoduck population densities
is displayed in Table VI—il. The Green Point and Dungeness Bay
leasable beds have substantially higher population densities
than does the lowest density leased bed (Von Ge].dern Cove),
though they are of lower population density than the average
density of all leased geoduck beds.
Intertidal: Three beaches surveyed in the Harbor are known to
support a minimum of 12 species of commercial and/or non—commer-
cial clam species (Table VI-12) (Bishop and Devitt 1970; Kittle
1976). The beaches surveyed (Figure VI—8) are not directly com-
parable due to habitat and substrate differences:
• Beach #1 was primarily a wave swept, loose pea
gravel habitat; there was little in the way of
clam habitat, and zero live clams were found
(1969 survey revealed areas of black sludge).
• Beach #2 was sand and mud below a rocky tide zone.
The west end of the beach was sandy. This condi-
tion changed to an impervious sandstone clay sub-
strate approximately 2500t east of the U.S. Ferry
Terminal (1969 survey revealed minor quantities
of black sludge).
• Beach #3 substrate varied from bay mud near the
Pilot boat dock to a gravel sand mixture near the
eastern end of Ediz Hook. Some sludge was observed
on the public boat launch and in the immediate
vicinity of Pilot boat dock (1969 survey revealed
no black sludge in the area).
289

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Table VI-li. GEODUCK POPULATION DENSITIES
Source: Goodwin 197.8
Location
Notes
Density:
geoduck/ft 2
Green Point (west)
whole bed
0.078
Green Point
leasable bed
0.133
Green Point (east)
whole bed
0.063
Dungeness Bay
whole bed
0.086
Dungeness Bay
leasable bed
0.116
Port Gamble
highest density
leased
bed
0.729
Von Geldern Bay
lowest density
leased
bed
0.029
--—
average density
leased
bed
0.187
Conversion 1 ft 2 = 9.29 in 2
290

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Table VI-12. NUMBER OF SPECIES SAMPLED AT EACH BEACH LOCATION IN PORT ANGELES HARBOR, WASH.
Beach
#1
Beach
#2
Beach
#3
1969
1975
1969
1975
1969
1
975
No. of Samples Taken 23
14
24
8
17
1].
CLAM SPECIES
Butter
( Saxidomus giganteas ) 0 0 0 0 10 2
Cockle
( Clinocardium nuttali ) 0 0 0 0 4 2
Horse
( Tresus capax ) - 0 0 0 5 4 21
Horse
( Tresus spp. ) 0 0 0 0 4 0
Native Little Neck
( Protothaca staminea ) 0 0 0 1 107 10
Bent Nose
( Macoma nasuta ) 3 0 12 17 10 25
Macoma
( Macoma spp. ) 0 0 1 0 0 0
Polluted Macoma
( Macoma irus ) 0 0 11 0 19 0
Eastern Soft Shell
( Mya arenaria ) 0 0 0 0 4 0
Truncate Soft Shell
( Mya truncata ) 0 0 0 0 1 4
Blunt Jackknife
( Solen sicarius ) 0 0 0 0 1 0
Tellen
( Tellina spp. ) 0 0 36 0 0 0

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Strait of Juan de Fuca
Figure VI-8. LOCATION
OF
PORT
ANGELES
HARBOR
INTERTIDMJ BEACH SAMPLES
L
Source:
Bishop & Devitt
1970;
Kitt].e
1976
— — I
EdIz Hook
S Transict
t$ 37
BEACH 3
* Wa$t• D schaigs
1959 Wansacts
(1975) Transcts
24 — 37
(25 —
Port Angeles Harbor
BEA(.H 2 15-23
(S — 24)
BEACH 1 1-14
(1-14)

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Despite the fact that fewer samples were taken during the 1975
study a comparisor. of genera]. data from the two studies can be
made as graphically displayed in Figure VI-9. Beach #1 is
an unsuitable clam habitat due to a high wave energy regime and
a shifting pea gravel substrate. No clams should be expected
to be found. Changes in shell weight density could be attri-
butable to tidal action and currents since few live clams were
found.
Beach #2 has some suitable clam habitat on the easterly 1,500
ft (457.2 m) , the westerly 1,000 ft (304.8 m) being an
impervious sandstone substrate. No explanation is apparent for
the increase in biomass and shell weight density on Beach #2
and none is offered by the original researchers.
Beach #3 showed little difference from 1969 to 1975 except for
shell weight density, for which no explanation is apparent.
No conclusion can be drawn from the data available either as
summaries or detailed tables. The survey has not yet been con-
ducted frequently enough or over a long period of time to be of
value. Due to substrate differences, the beaches are not them-
selves comparable.
Crustaceans: At least four crustacean species are conimercially
and recreationally harvested in the Port Angeles — Dungeness
area (Dungeness crab, coon shrimp, 2 species of pink shrimp).
The commercial crab fishing season is open from October 1 through
April 15 whereas recreational crab fisheries occur from June 1
through April 15. Catch data for both seasons, from 1977 to 1979
is summarized in Table vI-13. Since this is crab catch data, var-
iance in the number of days the pots were fished each year,
reliance on fish tickets and reported landings may explain the
fluctuation in catch for each of the three years. There were
293

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LIVE CLAM
DENSITY
bIVMAb
C 4
E
4
SIILLL WEIGHT
DENSITY
— 1975
BEACH NUMBER
Figure VI-9.
COMPARISON OF 1970 CLAM SURVEY TO 1975 CLAM SURVEY
I
B
1 2 3
BEACH NUMBER BEACH NUMBER
1
2
1
—197o
21.B
3
Source: Bishop & Devitt 1970; Kittle 1976

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Table VI-13. COl ’1MERCIAL AND RECREATIONAL CRAB CATCH FOR
DUNGENESS BAY, WASHINGTON (1975 - 1978)
Source: Bumgarner 1977 and 1979
Date
Commercial
Total Catch
(ibs)
Date
Recreational
Total Catch
(ibs)
10/1/75 —
4/15/76
35,918
6/1/75 —
4/15/76
31,276
10/1/76 —
4/15/77
20,454
6/1/76 —
4/15/77
22,103
10/1/77 —
4/15/78
10,531
ND
ND
ND - no data
Table VI-14.
COMMERCIAL SHRIMP
HARBOR, WASHINGTON
CATCH DATA FOR PORT
(1975, 1977 — 1978)
ANGELES
Source: Bumgarner
1977 and 1979
Date
Total Catch
(ibs)
4/15/75 —
9/30/75
353
4/15/77 —
10/15/77
385
4/15/78 —
10/15/78
977
295

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no catch data provided on the Harbor but DNR (1977) indicates
commercial fishing for Dungeness crab does exist in the area.
The Harbor supports a very small commercial shrimp fishery,
in comparison to other areas in Puget Sound (Table vi-14).
All catch data was retrieved from fisherman using shrimp pot
gear.
D. OTHER MARINE INVERTEBRATES
Surveys or studies directed toward sampling invertebrate
organisms in general are discussed in this section. Unlike
the previous section (C), no one specific type of invertebrate
(i.e. shellfish) is surveyed; therefore study results reveal a
variety of invertebrate species in the area from the Harbor to
Dungeness Spit.
Marine invertebrates are predominately benthic (within the
bottom sediments) and epibenthic (on or near the bottom surface),
occupying bottom habitats extending from the high tide mark
to deep waters. These organisms are able to adapt to rocky,
sandy, or muddy substrates which are typical of waterways and
shorelines in the Pacifc Northwest. Benthic invertebrates
vary in size from a few millimeters to several decimeters.
Limited studies in the Harbor and adjacent waters have revealed
known types of benthic, epibenthic or pelagic (open water) inver-
tebrate species. These invertebrates were surveyed in the lit-
toral and sublittoral zone. For the purposes of this discussion,
littoral habitats are defined to include shoreline waters to
a depth of roughly 15 feet (4.6 m) with the sublittoral zones
comprising all deeper waters.
The following information is sectioned into two major parts. Sub-
section (1) provides a brief discussion on invertebrate studies
296

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and corresponding methodologies conducted in the Harbor and
adjacent waters (1964 - 1978). The subsequent subsection (2)
summarizes the results of each individual littoral and sub-
littoral study in reference to determining a) abundance of
benthic and epibenthic invertebrates or b) sludge bed effects
on existing populations.
1. Invertebrate Survey Methods
Since 1964 invertebrate surveys and sampling in the Port
Angeles area have been conducted by federal (Federal Water
Pollution Control Administration (FWPCA)), state (wPCC),
and private agencies or corporations (Crown Zellerbach Corp.,
ITT Rayonier Inc., NTPC and Friday Harbor Laboratories (FHL)
and the Fisheries Research Institute (FRI) of the University of
Washington) (Table VI-15). During each study marine invertebrates
were sampled from the littoral and/or sublittoral zone. The
sample location determined the sampling methodology for each
survey (Table VI—15). Since epibenthic organisms are also
surveyed during benthic sampling, the term benthos as used
here refers to both groups of invertebrate fauna (epibenthic
and benthic) unless indicated differently.
During the 1960’s ITT Rayonier conducted invertebrate surveys
of those species inhabiting the mill’s dock pilings (Stein and
Denison 1966). In addition to removing the species from the
pilings for identification, SCUBA divers also utilized direct
observation and photography.
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) ini-
tiated a four year study (1962 - 1966) to investigate water
pollution in four areas of Puget Sound (USD1 1967). In coop-
eration with this project, the benthic fauna of the Harbor was
surveyed (September 30, 1964) in conjunction with sludge deposits.
297

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Table VI-15. MARINE INVERTEBRATE STUDIES CONDUCTED IN THE PORT ANGELES AREA
Invertebrates
Agency Study Date Sampled Location Methodology Source
ITT Rayonier 1961 — 1962, encrusting littoral observation & Stein & Denison,
1964 — 1966 sublittoral scraping 1966
WPCC, FWPCA Sept. 30, 1964 epibenthic & sublittoral van Veen dredge USD1 1967
benthic
Crown Zellerbach January 1972 epibenthic & sublittoral van Veen dredge English 1972
benthic -
FRI, University of May 1976 - pelogic, epiben- littoral fish seine and Simenstad etal.1977;
Washington June 1978 thic & benthic sublittoral townet Cross et al. 1978
FHL, University of Spring 1976 — epibenthic & littoral 2
Washington Winter 1978 benthic sublittoral .25 in 2 and .05 m Nyblade 1978;
frames van Veen Nyblade 1979
dredge
NTPC February & epibenthic & littoral .025 M 2 and .05 in 2 NTPC 1979
April 1978 benthic sublittoral Ponar grab

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On September 30, 1961 bottom samples were collected with a 0.25
cubic foot van Veen dredge from 31 sublittoral sites in the
Harbor (Appendix VI-F, Figure VI-F-l). A portion of each sam-
ple was analyzed for volatile solids and the remainder was washed
and screened previous to the identification of bottom dwelling
invertebrates. “Organisms were classified as to kind, each
kind being a group of organisms having similar life zones and
food habits (USD1 1967).lt The Harbor’s sludge composition was
determined from 22 core samples taken near ITT Rayonier and the
western portion of the Harbor.
During 1971 three surveys were conducted on the sludge beds
adjacent to Crown Zellerbach’s loading dock to determine their
depth, extent and activity (Aspitarte and Smale 1972). In
conjunction with these sludge bed surveys, benthic invertebrates
were also sampled from 18 stations (January 19 — 20, 1972) (Fi-
gure VI—F—2) (English 1972). The purpose of the benthic study
was to duplicate the 1964 (USD1 1967) survey methods and sample
sites (western portion of the Harbor only) to allow for a compar-
ison of benthic organisms obtained in each of the two surveys
(English 1972)
A 0.11 cubic foot van Veen dredge was used to sample 18 stations
in the Harbor. A portion of each sample was analyzed for vola-
tile solids while the remainder was screened through a 1 mm mesh
to retain the benthic invertebrates for identification.
In anticipation of oil shipments through the Strait, a series of
baseline studies were initiated in May 1976 through the Puget
Sound Energy - Related Research Project. One two year study (Si-
menstad et al. 1977, Cross et al. 1978) determined the distribu-
tion, abundance, biomass, and food habits of nearshore fish and
identified incidental marine rnacroinvertebrates collected with
the fish. The littoral zone was sampled with a beach seine and a
townet was used in the sublittoral zone. Benthic species were
collected only by the beach seine and pelagic species occurred
in the townet hauls; however, epibenthic fauna occurred in both
beach seines and townets (refer to Section VI.E.i. for further
discussion on methods).
299

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During the two year study (May 1976 - June 1978) ten sites
along the southern shores of the Strait (Neah Bay to Alex-
ander’s Beach) were sampled for fish and invertebrates. Only
two locations were sampled in the waters from the Harbor to
Dungeness Spit (Figure VI-F -3).
A baseline study initiated in response to potential oil ship-
ments (Nyblade 1978, 1979) was conducted to quantitatively and
qualitatively identify the epibenthic and benthic marine inver-
tebrates inhabiting the intertidal (littoral) and shallow sub-
tidal (sublittoral) areas of 10 selected sites along the Wash-
ington coastline of the Strait. The seasonal invertebrate com-
position of each sample site and the vertical distribution of
each species were also studied. Of the 10 sample sites (Kydaka
Point to North Beach), only Morse Creek and the Dungeness Spit
sites are located in the study area (Figure VI-F-3).
During the first year study (spring 1976 - winter 1977), abun-
dance data was collected seasonally from +6.0 ft., +3.0 ft.,
0.0 ft., -16.4 ft., and -32.8 ft. tidal heights. Data on the
distribution of organisms were collected only during the summer
from sites located at one foot tidal height increments from
0.0 ft. to —32.8 ft. The second year’s study (spring 1977 -
winter 1978) concentrated sampling efforts only in the +6.0 ft.,
+3.0 ft., 0.0 ft., —16.4 2 t, —32.8 ft. tidal heights.
Morse Creek and Dungeness Spit were sampled as described (Nyblade
1979)
Morse Creek — intertidal (0.0 ft. to splash zone) cobble:
Four 0.25 m 2 quadrats, each consisting of five 0.01 m 2
subsection scrapes, the residual 0.2 In 2 scrape, and the
under-cobble 0.05 m 2 x 15 cm sediment core fixed and dead-
sieved through 1 mm mesh; four 0.25 m 2 x 30 cm deep quad—
rats live-sieved through 12.5 mm mesh.
Dungeness Spit - intertidal (Exposed Gravel and Sand):
Five quadrats of 0. 5 m 2 x 15 cm deep sediment cores
fixed and dead—sieved through 1 mm mesh; five of 0.25 m 2
x 30 cm live -sieved through 12.5 mm mesh.
300

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Morse Creek and Dungeness Spit — soft sediment -
subtida (below 0.0 ft. tide): Two quadrats each
a 0.1 m van Veen grab sample partitioned on the
boat into equal halves.
The collected specimens were identified and counted.
The main purposes of the NTPC’s (1979) invertebrate study were
to 1) characterize 14 selected littoral habitat types from
Freshwater Bay to Port Townsend, 2) quantitatively assess the
littoral invertebrate types at 3 locations and sublittoral
organisms along primary and secondary submarine pipeline routes,
and 3) study the intertidal and subtidal shellfish in the Har-
bor (NTPC 1979). The habitat classification locations and the
sampled littoral and sublittoral sites located between the
Harbor and Dungeness Spit are shown in Figure VI—F-3.
The intertidal or littoral beaches (Figure VI-F-3) were clas-
sified in April 1978 in accordance with the DOE classification
system. Beaches were characterized according to the following
habitat types: rock, sand, mud, mixed fine, mixed coarse and
salt marsh.
Two sites in the study area were sampled for littoral inverte-
brates during February and April 1978. Three tidal levels
(+6.0 ft., +3.0 ft., and +1.0 ft.) were sampled in April but
only 2 tidal levels (+6.0 and +3.0 ft.) were sampled in Febru-
ary. Each littoral site was sampled for benthic invertebrates
as shown below:
Morse Creek: Four .25m 2 quadrats, each consisting of
five 0.01 m 2 subsection scrapes, and infauna 0.05 m 2 x
15 cm sediment core fixed and dead sieved through 1 mm
mesh before identifying.
Dungeness Spit: Five quadrats (three for Jamestown) of
0.05 m 2 x 15 cm deep sediment cores fixed and dead sieved
through 1 mm mesh before identifying.
The six sublittoral stations (Figure VI-F-3) were sampled with
a 0.05 m 2 Ponar grab. The best three of five samples based on
constant volume were preserved and dead sieved through a 1 mm
sieve.
301

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2. Marine Invertebrate Survey Results
The occurrence and population data on benthic and epibenthic
invertebrates collected during a study are closely related
to the type of habitats that are sampled during the survey.
Since benthos do live within or on the surface of bottom
sediments, substrate type will often determine the species
of benthos capable of inhabiting an area. The littoral and
sublittoral areas in the Harbor and adjacent waters are composed
of a variety of habitat types (refer to Figure VI—F-3 for loca-
tions). The most common littoral habitats found in the Harbor,
as well as along the eastern Strait are mixed coarse (sand
and cobbles), mixed fine (sand and gravel) and mud (NTPC 1979).
From Morse Creek to Green Point the beaches are composed of
mixed coarse or cobble (INTPC 1979). Mixed fine or gravel are the
major substrates for Ediz Hook, the beach immediately west
of ITT Rayonier, and Dungeness Spit. The littoral areas of
Dungeness Bay and Jamestown are composed of sand and mud (NTPC
1979). The beaches at Morse Creek and Dungeness Spit have mod-
erate and high exposure respectively (Cross et al. 1978).
There are five major sublittoral habitats that occur in the
vicinity of the Harbor. These are mud, mixed coarse, mixed
fine, kelp and eelgrass (NTPC 1979). Extensive mud flats are
located in the harbor. Mixed coarse substrates dominate the
sublittoral areas between Morse and Siebert Creek (16 - 33 ft
depth (4.9-10.1 m) and also occur in reduced quantities in the
area of Dungeness Spit and Ediz Hook (NTPC 1979). The locations
of kelp beds and eelgrass beds are shown in Figure VI-4, Sub-
section VI.A.2. In the eastern part of the Harbor extensive
sludge beds exist; whereas those beds on the east and west
sides of ITT Rayonier are slowly dissipating (Moore 1976).
Invertebrate Abundance, Species Richnese and Divex’eity: Exist-
ing data indicates two areas (Morse Creek and Dungeness) located
302

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between the Harbor and Dungeness Bay have been quantitatively
and/or qualitatively surveyed for benthic and epibenthic inver-
tebrates in the littoral and sublittoral zones (Nyblade 1978,
1979 and NTPC 1979). Invertebrates from these same areas were
also sampled incidentally during fish beach seines and tows
(Sinienstad et al. 1977; Cross et al. 1978). Qualitative and
quantitative differences in the incidentally collected data
cannot be compared with other surveys; therefore FRI survey
results (Simenstad et al. 1977; Cross et al. 1978) were only
utliized to complete an invertebrate species list for the study
area.
A minimum of 205 identified macroinvertebrate (larger than 1 mm)
species occurred in the waters and beaches from within the Harbor
to Dungeness Spit (Appendix VI-G, Table VI-G-l). The inverte-
brates sampled from ITT Rayonier’s dock pilings are provided in
Table VI-G—2. Ten identified invertebrate species were collected
only on the pilings while the remaining six occurred in both the
bottom habitats of the study area and on the mill’s pilings (Tables
VI-G-l, VI-G-2). Ninety-eight benthic and epibenthic species were
identified along the shallow beach areas (+7.0 ft. to -16.4 ft.)
of Morse Creek and Dungeness Spit (Table VI—G—1). The distribu-
tion and abundance of these littoral invertebrates is dependent,
among other things, on their location above or below mean lower
low water (MLLW), the substrate type and the substrate stability
(NTPC 1979). A comparison of the species richness (number of
species/study area stratum/sampling period) indicates the Morse
Creek cobble beach supports a more abundant population of benthic
invertebrates than the exposed, unstable coarse beach of Dungeness
Spit (Table VI—16) (Nyblade 1979; NTPC 1979). Intertidal species
(+0.6 ft to 0.0 ft) also increased with decreasing tidal height
(Table VI—16) (Nyblade 1979; NTPC 1979).
Species diversity is a better indication of community complexity
than species richness. This reflects both the species number
and the evenness of their occurrence. A community having a
relatively even quantity of organisms representing each species
303

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Table VI-16.
SPECIES RICHNESS AND DIVERSITY OF BENTHIC AND EPIBENTHIC LITTORAL INVERTEBRATES
COLLECTED AT MORSE CREEK AND DUNGENESS SPIT, SPRING 1976 - WINTER 1978
Source: Nyblade 1978; Nyblade 1979
LITTORAL ZONE
Date
Spring 1976
Summer 1976
Fall 1976
Winter 1977
Spring 1977
Summer 1977
Fall 1977
Winter 1978
+0.6
SR D
11 1.33
5 0.54
8 0.23
10 1.78
8 1.31
16 0.76
7 0.48
15 1.72
Morse Creek
Tidal Height (feet)
+0.3
SR D
51 1.56
61 1.55
62 2.11
53 2.12
59 2.34
76 2.04
70 1.97
64 2.50
+0.0
SR D
109 2.80
134 2.68
90 2.47
74 2.62
112 2.14
117 2.55
82 2.29
N/D N/D
+0.6
SR D
4 0.88
6 1.50
2 0.69
0.0 0.00
2 0.69
1 0.00
0.0 0.00
1 0.00
Dungeness Spit
Tidal Height (feet)
+0.3
SR D
7 0.90
4 0.49
2 0.45
+0.0
SR D
30 2.44
2 0.69
0.0 0.00
1 0.00
3 0.69
2 0.13
5 0.27
1 0.00
SR — Species Richness
D — Diversity
N/D- no data
0.0
2
2
1
1
0.00
0 • 08
0.56
0.00
0.00

-------
is more diverse than one with an equal number of species but an
overwhelmingly high number of organisms per species for a few
species (Nyblade 1978). As with species richness, diversity in
the littoral zone is higher atMorse Creek than Dungeness Spit
and increases withdecreasingtidal height (Table VI—16).
A minimum of 140 benthic and epibenthic organisms occur in the
sublittoral waters from the Harbor to Dungeness Bay (Table VI—F-1).
Species richness and diversity of sublittoral areas off Morse
Creek and Dungeness Spit are much higher than their respective
littoral beach habitats (Tables VI—16, VI—17) (Nyblade 1978, 1979).
The sublittoral areas sampled from the Harbor to Dungeness Bay
by NTPC (1979) does not indicate if the same depths were sampled
at each location; therefore the species richness and diversity
data is not comparative (Table VI—l7).
Nyblade (1978, 1979) summarized survey results on the dominant
benthic and epibenthic species collected at Morse Creek and
Dungeness Spit in reference to feeding types (Table VI—18,
VI-19). The majority of the invertebrates are represented by
detritivores. Due to the type of feeding habits utilized by
marine invertebrates, pollutants introduced to the receiving
waters may directly or indirectly affect the population of the
organism. This topic is further discussed in Chapter VIII.
Sludge Beds: In the Harbor the discharge of volatile solids
by Crown Zei.lerbach, Fibreboard and ITT Rayonier resulted in
an oxygen deficient layer of decomposing organic material ref er-
red to as sludge beds (Figure VI-lO, VI-li). Due to the closure
of Fibreboard and the treatment systems installed by Crown
Zellerbach and ITT Rayonier, significant sludge bed build up
has ceased in the Harbor but the beds do continue to exist.
According to Moore (1976) those beds in the eastern Harbor have
not changed since 1961; however wave action is slowly causing
the beds surrounding ITT Rayonier to recede.
Deposits of sludge often have a deleterious effect on the natu-
ral benthic community. Sludge deposits physically alter the
305

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S - spring
W - winter
N/D - no data available
(a) — refer to Figure VI-F—3
SR - Species Richness
D - Diversity
* winter (February 1978)
** spring (April 1978)
Table VI-l7. SPECIES RICHNESS AND DIVERSITY OF BENTHIC AND EPIBENTHIC SUBLITTORAL INVERTEBRATES
COLLECTED FROM THE HARBOR TO DUNGENESS BAY, SPRING 1976 - SPRING 1978
Source: Nyblade 1978 & 1979; NTPC 1979
SUBLITTORAL ZONE
Morse Creek
Tidal Height Cf t)
Dungeness Spit
Tidal Height Cf t)
Harbor to
STATION
Dungeness
LOCATIONS
Bay
(a)
—16.4
—32.8
—16.4
—32.8
1
2
3
5
6
7
Date SR
D
SR
D
SR
D
SR D
SR D
SR
D SR
D SR
D SR D
SR D
S 1976 74
3.01
149
2.79
30
2.44
90
2.97
N/D
MID
MID
N/D
MID
N/D
N/D
MID
M iD
N/D
N/D
N/D
S 1977 N/D
MiD
127
2.72
28
2.43
136
3.82
N/D
N/D
N/D
HID
MID
HID
MID
N/D
N/D
N/D
N/D
N/D
W 1978* MID
N/D
MID
MID
N/D
MID
N/D
HID
52
2.90
70
4.69
43
3.29
75
4.82
63
3.69
52
3.43
S l978 N/D
MID
N/D
N/D
MiD
N/D
N/D
MID
67
4.31
45
4.20
36
3.20
77
4.95
63
3.55
46
4.26

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Table VI-18. DOMINANT BENTHIC LITTORAL ORGANISMS SAMPLED AT MORSE CREEK
AND DUNGENESS SPIT, SPRING 1976 - WINTER 1977
Source: Nyblade 1978 & 1979
Zone
LITTORAL ZONE
Morse Creek
Feeding type Organism
Dungeness Spit
Feeding type
Organism
+6.0
Detritivores
Oligochaetes
Detritivores
Oligochaetes
“
Isopods
Amphipods
‘I
Gammarid amphipods
Suspension feeder
Barnacles
+3.0
Grazers
Gastropod
Detritivores
Oligochaetes
—-
Idotea
Amphipods
Suspension feeder
barnacles
Detritivores
“
Hemigrapsus
Pagurus
“
“
“
Capitella
Malacoceros
Corophium
+0.0
Herbivores
‘I
“
Lacuna
Not5acmea
Detritivores
Oligochaetes
Amphipods
Pugettia
Detri tivores
“
“
“
“
Nematodes
Abarenicola
Capilella
Cirratulus
Armandia
“
Spionids
“
“
Leptochelia
Gammarid amphipods
Herbivore
Nereis
Suspension feeder
“.
“
Predator
Protothacu
Tresus
Sabellids
Thais spp.
“
Cance spp.

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Table VI-19. DOMINANT BENTHIC SUBLITTORAL ORGANISMS SAMPLED AT MORSE
CREEK AND DUNGENESS SPIT, SPRING 1976 - WINTER 1977
Source: Nyblade 1977 & 1978
Zone
SUBLITTORAL
Morse Creek
Feeding type Organism
ZONE
Dungeness Spit
Feeding type
Organism
—16.4
N/D
N/D
Suspension feeder
“
“
“
Detritivores
Mysella
Crennella
Psephidia
Leptochelia
dubia
Gammarid
amphipods
—32.8
Detritivores
.
Macoma
Cepitellids
Detritivores
“
Capitellids
Dorvilleids
“
Maldanids
I’
Spionid
I’
Armandia
Syllids
“
Spionids
Gammarid
“
Exogone
amphipods
°
Gammarid amphipods
Macoma spp.
“
Ophiuroids
Suspension feeder
Mysella
Suspension feeder
“
Ca lyptraea
Crennella
Leptochelia
Crennalla
“
Mysella
Psephidia
“
Leptochelia

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Strait of Juan de Fuca
Crown
Zel lerbach
Corp.
0 —
— —
I
PORT ANGELES
1 ,dk I mile
I
/
/
I
jure VI-lO. THICKNESS IN INCHES AND AERIAL DISTRIBUTION OF
SLUDGE DEPOSITS, SEPTEMBER 30, 1964
)
Source: USD1 1967

-------
Strait of Juan de Fuca
Crown
Zel $erbach
Corp .
ANGE LES
(Fi ure VI-il.
DISTRIBUTION OF PERCENT VOLATILE SOLIDS IN THE SLUDGE
AND BOTTOM SEDIMENTS IN PORT ANGELES HARBOR, 9/30/64
Source: USD1 1967

-------
substratum, eliminating many of the indigenous organisms
through burial and suffocation. In some cases, decomposition
of the organic material causes depletion of dissolved oxygen
sulfide and ammonia. These conditions often eliminate all
traces of benthic life.
In 1967 subsequent to a study on sludge beds and benthic fauna
(September 30, 1964), the Washington State Enforcement Project
(USD1 1967) concluded that damage to the benthic community occur-
red in areas (1 — 4) covered by one inch of sludge or more
(Figure VI—lO, VI-12, and Table VI-20). The volatile solids
content in these areas (1 — 4) was 7% greater (Figure VI-il,
Table VI-20). Substantial quantities of pulp fiber were also
found in these areas (USD1 1967).
In 1971 (October 13 — 14, 1971) sludge bed survey results con-
ducted adjacent to the Crown Zellerbach mill showed sludge depths
ranging from 2 ft (.61 m) to 20 ft (6.1 m) or more (Figure VI—
(Aspitarte and Smale 1971, survey 1). Volatile solids for this
same area are described in Figure VI-14. In conjunction with
the October survey, on January 18 and 19, 1972, bottom organisms
and volatile solids were sampled in this area and adjacent areas
from locations that were sampled during September 30, 1964
(English 1972). In areas immediately adjacent to the mill
(sta-
tions 1, 2 and 3), 1972 volatile solids measurements were relatively
comparable (station 1) or significantly higher (stations 2 and 3)
than those of 1964 (Figure VI-F-2, Table VI-21, Figure VI-15).
Before a comparison can be made between the federal government’s
benthic survey (September 30, 1964) and Crown Zel].erbach’s benthic
survey (January 18 and 19, 1972) the following differences in
methods should be recognized:
1. The federal study used a 0.25 cubic foot van Veen
grab; whereas Crown Zellerbach used a 0.11 cubic
foot grab sampler.
2. The federal study was conducted in September; Crown
Zellerbach’s study was initiated in January.
311

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11
Crown
Z•lI.rbach
Corp.
J
FIbr.bo.rd Papir
Products Corp.
9
.
“ —iii AREA 2
cii i
—iiiiii
Substautial Damag to Bnthic Community
Som. DSm.g. to S.nthlc Community
• S.nth lc Sampling Station
PORT ANGELES
Nautical Nil.
Figure vi-12.
BENTHIC SAMPLING STATIONS IN PORT ANGELES HARBOR ON
SEPTEMBER 30, 1964; AND AREAS OF DAMAGE TO THE BENTHIC
COMMUNITY (Aspitarte and Smale 1971)
ST! IT OF JUAN DE FUCA
10
.
12
•
16
I
17
.
15
•
18
•
AREA
19
I
14
•
21
•
20
•
22
•
24
23
I
ITT
I
Ryonlsr
Inc.

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Table vi-20. RELATIVE NUMBERS AND KINDS OF BENTHIC ORGANISMS, AND PERCENT VOLATILE SOLIDS IN
SEDIMENT SAMPLES COLLECTED IN PORT ANGELES HARBOR ON SEPTEMBER 30, 1964.
Source:
USD1 1967
Relative Number* of Each
Kind per
Sample
Total
Relative
Kinds
% Volatile
Solids
Crabs
Amphipods Clams Copepods
Shrimp
Moss
Number*
per
in the
Area
Station
Worms
Isopods Snails Ostracods
Cumaceans
Animals
Other
Per Sample
Sample
Sediment
1
1
0
0
68
2
0
0
20
3
1
1
1
14
4
2
1
3
2
26
5
2
1
3
2
16
2
6
3
1 1
5
3
19
7
4
1 2
7
3
9
8
2
4 1
7
3
21
Main 9 4 2 4 2 12 4 18
Area 10 4 1 2 2 9 4 19
of 11 5 3 1 1 1 11 5 9
Harbor 12 5 4 1 1 1 12 5 9
13 4 2 1 1 8 4 10
14 4 5 4 3 16 4 6
15 4 1 1 1 3 1 1 12 7 5
16 5 3 1 3 12 4 5
17 4 4 3 4 1 1 17 6 5
18 3 5 1 1 10 4 28
19 3 5 2 1 11 4 7
20 2 5 1 1 9 4 6
21 4 3 2 1 10 4 5
22 4 5 2 1 12 4 5
23 3 5 3 3 14 4 5
24 2 5 1 2 1 11 5 4
25 5 1 2 1 9 4 3
3 26 2 3 5 2 21
27 4 4 2 10 3 9
28 3 4 5 12 3 27
29 4 4 1 9 3 8
4 30 0 0 61
31 C) 0 7
*Assigned rank values are Abundant(S), Common (4), Few (3), Scarce (2), Rare (1), None (blank or 0).

-------
(Fi ure VI-13.
THICKNESS IN FEET AND AERIAL DISTRIBUTION OF SLUDGE
DEPOSITS ADJACENT TO CROWN ZELLERBACH COBP q PORT
ANGELES HARBOR OCTOBER 13 & 14, 1971
Source: Aspitarte &Smale 1971
3

-------
Strait of Juan de Fuca
Crown
Zel lerbach
Corp.
ANGE LES
— — — — —
— — — ____
Figure Vi-14. DISTRIBUTION OF PERCENT VOLATILE SOLIDS IN THE SLUDGE
AND BOTTOM SEDIMENTS ADJACENT TO CROWN ZELLERBACH CORP.
PORT ANGELES HARBOR, OCTOBER 13 .& 14, 1971
Source: Aspitarte & Smale 1971

-------
Strait ol Juan do Fuca
Crown
Zel lerbach
Corp.
ANGE LES
C Figure VI-15. DISTRIBUTION OF PERCENT VOLATILE SOLIDS IN THE SLUDGE
AND BOTTOM SEDIMENTS IN EASTERN PORT ANGELES HARBOR,
JANUARY 18 & 19, 1972

-------
Table vi-21. COMPARISON OF PERCENT VOLATILE SOLIDS IN
BENTHIC SAMPLES TAKEN ON SEPTEMBER 30,1964
AND JANUARY 19 and 20, 1972 IN EASTERN PORT
ANGELES HARBOR, WASHINGTON.
Source: English 1972
Stations
% Volatile
Solids
1964
1972
1964
1972
1
1
68.0
54.2
2
2
20.0
44.3
3
3
14.0
52.0
—
4
——
39.8
—
5
——
31.6
4
6
26.0
32.5
5
7
16.0
13.4
—
8
——
30.7
9
9A
18.0
7.0
—
10
——
21.9
7
11
9.0
9.2
6
12
19.0
12.6
8
13
21.0
27.3
—
16
5.0
10.0
13
17
10.0
5.5
317

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3. The federal study provided their organism counts
as abundant, common, few, scarce, rare and none.
Crown zellerbach provided absolute counts.
Despite the fact the 1964 samples were 2.2 times larger than
the 1972 samples, area 1 surveyed in 1972 showed more kinds
of benthic species than 1964 results (Tables VI—22, VI—23).
During both survey years (1964, 1972) more kinds of benthic
invertebrates were present in the main Harbor area than in
area 1; however in 1964 the main Harbor area differed by a
factor of 4 and in 1972 the difference was approximately 2
(Table VI-23). Comparing the relative abundance counts of
1964 with the absolute counts of 1972 is difficult (areas 1 &
2, main Harbor). A comparison of these counts does show that
the somewhat uniform counts for each area (1 & 2, main Harbor)
in 1964 were not the case in 1972 (Table VI-23). Unlike the
1964 results, in 1972 stations in areas 1 and 2 had more ben—
thic invertebrates than some stations in the main Harbor area
(Table VI—23).
The author concluded from these results that from 1964 to 1972
the environment for benthic invertebrates in the eastern Harbor
improved in some areas where sludge beds exist (English 1972).
This was attributed to natural processes which reduced and
should continue to improve the adverse effects of the sludge
beds in these areas (English 1972).
E. FISH
There are a total of 12 tributaries contributing direct flows
to the study area (Elwha River east to the Dungeness River).
Each of these tributaries support one or more species of anadro—
mous salmon end/or trout during the freshwater stages of their
life cycles. In addition to anadromous fish, 61 marine fish
species have been sampled or surveyed in the study area.
318

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Table VI22. ABUNDANCE OF BENTHIC ORGANISMS IN NINE CATEGORIES TAKEN BY VAN VEEN
GRAB IN EASTERN PORT ANGELES HARBOR, WASHINGTON, JANUARY 19 & 20, 1972
Source: English 1972
.
Stati
°r
Worms
Worm
Frag.
Worms +
Frag.
Amph.
Isopod
Clams
Snails
Copep.
Ostra.
Crabs
Shrimp
Cumac
Moss
Animals
Other
Area 1964
1972
1 ——
——
——
A
B
C
30
1
4
3
33
1
4
1
1
1
1
9
9
2
3
——
2
3
4
1
6
2
1
8
13
1
8
——
5
4
5
6
7
8
1
9
1
6
1
1
2 ——
8
16
5
21
10
1
——
7
6
10
1].
12
3
1
2
2
5
3
9
1
5
29
4
2
1
Main 8
HarbO
——
13
9A
16
1
8
14
1
3
6
11
20
2
3
1
4
4
13
17
24
8
32
2
27
2

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Table VI-23. NUMBER OF KINDS AND RELATIVE ESTIMATED NUMBERS OF BENTHIC INVERTEBRATES
IN 1964 AND TOTAL COUNT IN 1972 FOR STATION LOCATIONS IN EASTERN PORT
ANGELES HARBOR, WASHINGTON
Source: English 1972
Stations
Kinds per
Sample
Average
1964 1972
Abundance (a)
Relative Absolute
1964 1972
1964
1972
Area
1964
1972
1
1
1
0
1
0
9
——
A
1
33
--
B
2
2
--
C
2
5
•2
2
0
0
0
0
3
3
1
2
1.0 1.6
1
2
——
4
3
29
4
6
2
0
3
0
——
5
0
0
5
7
2
5
3
18
2
6
12
3
4
5
9
7
11
3
4
7
45
——
10
1
3.0 2.8
5
——
8
3
32
8
13
3
2
7
2
Main
HaO
9
10
——
9A
--
16
4
4
3
3
4.0 3.3
12
9
17
27
13
17
4
4
8
63
(a) refer to Table vI-20 for 1964 relative abundance

-------
Both marine and anadromous fish are important in nearshore
marine waters. 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 predate on lower organisms in the food chain and in
turn provide prey to some fish, mammals and birds.
Two major types of commercial fisheries occur in the study area.
These include trawling and salmon netting. Chinook, coho,
chum and pink contribute to the commercial and sport salmon
catch in the area. Significant bottom fish species in trawl
net landings include English sole, Dover sole, spiny dogfish,
Pacific true cod, Lingcod, and other rock fish.
The following information is divided into two major parts.
Subsection 1 provides a brief discussion on fishery studies and
corresponding methodologies conducted in the Port Angeles
region (1930’s — 1978). The subsequent subsection (2) sulTunar-
izes 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 and surveys in the Port Angeles area
have been conducted by federal (FWPCA), state (DOE, WPCC, WDF)
and regional (PNRBC) agencies, universities (FRI) and the pulp
and paper industry (ITT Rayonier) (Table VI-24) (see abbrevia-
tions, page iii). The sampling locations, equipment and method-
ology utilized in each study are briefly discussed in chrono-
logical order below. Surveys based on punch card or fish ticket
returns on anadromous and marine commercial and/or sport fish
species are not included in this section but are discussed under
research results (Section VI.2..d)
From the early 1930’s to 1975 survey counts of spawning salmon
were conducted in Washington tributaries. As of 1975, in
321

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Table VI-24. SUMMARY OF FISH SURVEYS CONDUCTED IN THE MARINE AND FRESHWATERS
FROM THE ELWHA RIVER EAST TO THE DUNGENESS RIVER
Agency Study Date Fish Type Methodology Source
WDF 1930’s — 1978 anadromous field investigation Egan 1978;1979;1980
WDF 1960 - 1978 anadromous hatchery return count Rasch & Foster 1978;
Foster et al. 1978
Fletcher etal. 1979
ITT Rayonier 10/12/61 anadromous beach seine Stein & Denison 1966
7/11/62 marine
9/1/64
6/29/65
7/26 — 7/27/65
8/2 & 8/6/65
7/12/66
WPCC and FWPCA April - May 1964 anadromous beach seine USD1 1967
PSTF of the PNRBC 1964 - March 1970 anadromous analysis of existing PNRBC 1970
data; field investiga-
tion
WDF 7/1/69 - 11/75 anadromous analysis of existing Williams et al. 1975
data; field investiga-
ti on
DOE 1974 - 1977 anadromous analysis of existing MSN 1977; DOE 1978
marine data
FRI 5/76 - 6/78 anadromous beach seine; townet; Simenstad et al. 1977;
marine tidepool analysis Cross et al. 1978

-------
addition to WDF, the United States Fish and Wildlife Service
(USFW), Washington State Department of Game (WDG) and several
Indian tribes also conducted salmon spawning counts in desig-
nated tributaries. Survey results are summarized by the WDF
(Egan 1978; Egan 1979).
The smaller streams were surveyed visually by walking the
stream to count spawning and/or dead adult salmon, or to con-
duct redd (salmon nest) counts. On larger rivers the visual
surveys were conducted by boat, plane or helicopter. In general,
it appears that environmental factors influencing the timing
of up stream migration were not a major determinant in the
scheduling of stream surveys; thus the data collected may not
be representative of actual salmon runs in streams infrequently
studied. These surveys (index counts), which cover only a por-
tion of the spawning area of a stream, provide relative escape-
ment (returning) counts for comparison from year to year (Egan
1979). Additional census methods (fish counting facilities,
hatchery rack counts, etc.) are required in order to obtain
a complete count of spawning salmon returning to a tributary.
The hatchery return counts (1960 - 1978) for the Elwha and
Dungeness salmon rearing facilities represent actual counts of
species returning to the hatchery (Rasch and Foster 1978;
Foster et al. 1978; Fletcher et al. 1979). These escapement
counts were composed by WDF from weekly counts conducted by
hatchery personnel (Rasch and Foster 1978).
On specific occasions during 1961 to 1966 nearshore fish sur-
veys were conducted by ITT Rayonier in conjunction with water
quality studies of the Harbor (Stein and Denison 1966). On
nine different occasions (1961 — 1966) beach seine samples were
taken at seventeen various locations east of ITT Rayonier
(Appendix VI-if, Figure VI-H-l). Collected nearshore fish were
identified and quantified. A seine haul was also conducted at
Dungeness but no station location was provided in the report.
323

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As a result of the joint federal — state Enforcement Confer-
ence (Olympia, Washington, January 16 - 17, 1962), a four
year comprehensive study was conducted by Washington State
Water Pollution Control Commission (WPCC) and the Federal
Water Pollution Control Administration (FWPCA) (Washington
State Enforcement Project) to investigate water pollution in
four areas of Puget Sound (USD1 1967). In cooperation with
this project, data on occurrence of juvenile salmon in the
Harbor was also collected (April - May 1964). Beach seine
samples were collected from five locations in the Harbor
(Figure VI—H-2). The 100 x 6 ft (30.5 x 1.8 m) bag-type
net was hauled parallel to the shoreline for 100 ft (30.5 m).
In 1964 the Puget Sound Task Force of the Pacific Northwest
River Basins Commission (PNRBC) initiated a water resource
study of the Puget Sound area (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 X I (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 et al. 1975)
describes the physical characteristics and salmon utilization
of major streams in a basin area.
The Washington Department of Ecology (DOE) conducted a marine
baseline study of northern Puget Sound from 1974 - 1977 (Gard-
ner 1978). Mathematical Sciences Northwest (MSN) participated
in this study by designating major biological significant areas
(critical habitats) for specific invertebrate, fish and bird
species along the Washington coasts which includes the Port
Angeles study area (MSN 1977). These areas were derived from
an anlysis of available information conducted by MSN. Further
324

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additions or corrections to the MSN (1977) report have been
incorporated into the Washington Coastal Zone Atlas (DOE 1979).
Designated critical habitats as defined by DOE were required to
possess at least one of the following criteria (MSN 1978; DOE
1978)
1. The area supports a population of species(s)
that not only consistently reproduces itself
but because of favorable environmental condi-
tions (currents, water temperature, salinity,
etc.), provides the major source of recruit-
ment for adjacent areas or regions whose pop-
ulations do not consistently reproduce them-
selves.
2. The area consists of a habitat type or types
that provide winter shelter, food or other
environmental necessities during a critical
part of a species life history. For example,
nesting sites or shelter from predators during
early life history stages.
Due to a limited data base and the subjective judgement of
biologists interpreting the data, the designated critical
habitat areas should not be interpreted as the only areas
which may exist (MSN 1977). Other state data which is
available in cartographic format is derived from the Washing-
ton Marine Atlas, published by the Department of Natural Resources
(DNR 1977); however, this is heavily biased toward commercial
species, since data is derived from commercial fishermen.
From 1976 to 1978 nearshore fish species were collected quarter-
ly from the Morse Creek area, the west end of Dungeness Spit
and 5 to 12 other sites along the Straits (Simenstad et al. 1977;
Cross et al. 1978) (Figure VI-H-3). A 120 foot (36.5 m) beach
seine with two wings (3cm mesh) joined to a 2.0 ft x 7.9 ft x
7.5 ft (0.6 m x 2.4 m x 2.3 m) bag (6mm mesh) was used to col-
lect demersal (bottom dwelling) nearshore species. The seining
was conducted during slack water at low tide (Cross et al. 1978).
Those neritic (pertaining to the shallow waters over the contin-
ental shelf) species occurring in the upper 11.4 ft (3.5 m) of
the water column adjacent to the shoreline were sampled with
a 10 x 20 ft (3.0 m x 6.1 m) townet. Net mesh size is graded
325

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from 3 inches (76.0 mm) to 0.25 inches (6.0 mm) at the bag.
Two 10 minute tows were conducted along the shoreline at each site,
one with the prevailing tidal current, the other in the oppo-
site direction. In the intertidal region (zone between high
and low water), tidepoo].s and areas beneath rocks were sampled
for fish.
Sampling techniques (beach seine, townet and intertidal sieving)
used to collect fish species were not 100% efficient. Small
fish and larvae were not entirely contained by net techniques
and faster swimming species avoided capture. Night sampling
(October through January) and day sampling (May through August)
may have resulted in a variance of fish fauna retrieved.
2. Fish Distributions and Research Results
a. Anadromous Fish Species Occurring in the Study Area
The coastal area from the Elwha River east to the Dungeness River
is the direct receiving water for 12 tributaries (Figure VI—16).
The streaxnbed and flow characteristics of each of those tribu-
taries is described in Appendix VI—I. These tributaries sup-
port major runs of one or more of the following anadromous spe-
cies:
Coho - Silver Salmon ( oncorhynchus kisutch )
Chum - Dog Salmon (0. keta )
Chinook - King Salmon (0. tshawytscha )
Pink - Humpback Salmon (0. gorbuscha )
Steelhead Trout ( Salmo gairdneri )
Searun Cutthroat Trout ( Salmo clarki )
Searun Dolly Varden Trout ( Salvelinus malma )
During salmon spawning counts, insignificant numbers of sockeye
or red salmon ( Oncorhynchus nerka ) occurred in the Elwha and
Durtgeness Rivers; however there is no major run of this species
in the area (PNRBC 1970; Williams et al. 1975).
326

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$ - Coho S.lmon
K- Chisooh S.knon
C — Chum $.lmon
P Pinli S mon
T St..lh..d,CuIIlWO .t.Sfld/Of Dolly Vs,dun
•— Ssknon Hatch.ry
—— Fish Batrist
Lowat us. lsttsa Indicits pobabl. use
STRAIT OF JUAN DE FUCA
P ot.cIIon
snd
ci
Figure v:r-16. INVENTORY OF SALMON UTILIZATION IN PORT ANGELES, WASHINGTON
Source: PNRBC 1970; Williams et al. 1975; Egan 1978; Egan 1979; Egan 1980

-------
The fresh water life cycle for six of these species is defined
according to location (Table VI-25). In order to spawn or
reproduce, the mature adult anadromous species migrates up-
stream in the fresh water tributary from which it originated.
Upon completion of the migration, the adult fish
utilizes gravel areas to deposit and fertilize eggs. Intra-
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) (USD1 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 closely assoc-
iated marine waters near tributary mouths. After adjusting
to the salt water environment, the fish will disperse to the
Strait and eventually the ocean (PNRBC 1970).
b. Inventory and Distribution of Anadromous Fish in Major
Tributaries Located Between the Elwha and Dungenes8 Rivers
Chinook Salmon: The Elwha and Dux geness Rivers support the
majority of spring and summer/fall chinook utilizing the trib-
utaries in the study area (Figure VI—16) (PNRBC 1970). Spring
chinook spawning is extensive in the upper reaches of the
Dungeness and Gray Wolf Rivers with limited use in the riffle
areas of the E].wha River below the Darn (PNRBC 1970). Summer-
fall chinook spawn throughout the Dungerless River and the
lower four miles of the Elwha River (PNRBC 1970). Due to their
small sizes and reduced flows during the summer and fall, the
remaining 10 tributaries may receive limited chinook use, es-
pecially in Morse Creek (PNRBC 1970; Williams et al. 1975).
Adult spring chinook begin migrating into the Dungeness and
Elwha River in mid-May and continue migrating through July
(Table VI-25). Spawning begins in August. Fry emerge from
the gravel and remain in the fresh water system until the fol-
lowing year when high spring run-off triggers their downstream
328

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Table VI-25. FRESHWATER LIFE CYCLE OF SALMON AND ANADROMOUS
TROUT SPECIES IN TRIBUTARIES FLOWING TO THE PORT
ANGELES AREA.
Source: PNRBC 1970; Williams et al. 1975
FRESH-WATER
SPECIES LIFE PHASE
—
— —
— —
J
F
14
A
14
3
3
A
S
0
N
D
Spring Upstream migration
Chinook spawning
Intragravel develop
Juvenile rearing
Juv. out migration
I
Summer- Upstream migration
Fall Spawning
Chinook Intragravel develop
Juvenile rearing
Juv. out migration
•
•
—
—
—
•
•
-
—
—
I
—
Coho Upstream migration
Spawning
Intragrave]. develop
Juvenile rearing
Juv. out migration
I
—
—
•
Pink Upstream migration
Spawning
Intragravel develop
Juvenile rearing
Juv. out migration
•
•
Chum Upstream migration
Spawning
Intragravel develot
Juvenile rearing
Juv. out migration
U
•
•
•
—
-
Summer Upstream migration
steelhead Spawning
Intragravel develop
Juvenile rearing*
Juv. out migration
—
—
—
—
—
a
a
—
I
*NorTJ 1ly extends over a two—year period.
329

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Table VI—25. continued
FRESH-WATER
SPECIES LIFE PHASE
Winter
steelhead
Upstream migration
Spawning
Intragravel develop
Juvenile rearing*
Juv. out migration
Searun
cutthroat
Upstream migration
Spawning
Intragrave ]. develop
Juvenile rearing*
Juv. out migration
*Normally
extends over a two year period.
330

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migration (Williams et a].. 1975)
Summer-fall chinook adults begin migrating up the Elwha
and Dungeness in late July and early August, respectively
(Table VI-25) (Williams et al. 1975). Following emergence
from the gravel, the majority of the fry remain in the rivers
for 3 months before their downstream migration (March to June)
(Williams et al. 1975).
The salmon spawning count conducted by WDF provide chinook
index counts for the Elwha and Dungeness Rivers and Morse Creek
(Table VI-J—l) but the lack of additional census data does
not allow the WDF to project total natural escapements (num-
ber of returning wild stock) for these tributaries (Geist,
personal communication of November 12, 1980). From 1965 to
1976 the WDF utilizing available data estimates that 1,550
wild stock chinook returned to tributaries located all along the
southern Strait (Neah Bay to Port Townsend) (Geist, personal
communication of November 12, 1980).
The WDF maintains two salmon rearing facilities in the study
area. The Elwha Salmon Channel (referred to as a hatchery)
is located on the E].wha River, 1.5 miles upstream from the
river’s mouth (Figure VI-16). This hatchery which began opera-
tion in mid-1975 handles both spring and fall chinook and coho.
The Dungeness State Salmon Hatchery is located at River mile
(from the mouth upstream toward the source) 10.5 on the Dunge—
ness River (Figure VI-16). Spring chinook, fall chinook, coho
and recently, pink salmon are spawned in this facility. The
total artificial escapement (returning hatchery stock) for spring
chinook (1960 — 1971) and fall chinook (1971 — 1979) to the
Dungeness Hatchery averaged 281 fish/year and 98 fish/year,
respectively (Table VI—J-3). A separate average for spring and
fall chinook returns to the Elwha Rearing Channel is not pro-
vided in the available information (Table Vi-J-3).
331

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Eggs are taken from these returning salmon, fertilized and
incubated in the hatchery facilities. Following hatching
the salmon are reared for a specified period before being
released or planted into appropriate tributaries. During
1977 and 1978 all spring and fall chinook artificially rear-
ed in the Elwha and Dungeness Hatcheries were planted in both
the Elwha and Dungeness Rivers (Table VI-J-4). Only fish
that had been reared for more than 269 days (yearlings) were
utilized for planting (Foster et al. 1978; Fletcher et al. 1979).
Utilizing salmon punch card data returned by anglers to WDF,
the Department annually estimates the fresh water sport catch
for salmon species caught in the Elwha and Dungeness Rivers
(Table VI—J-5). From 1973 to 1978 a total of 13 chinook were
reported to be caught from Elwha River and 223 from the Dunge—
ness River (Table VI—J-5).
Coho Sal mon: Coho salmon are known to utilize 7 of the
independent tributaries flowing directly to the receiving
waters between and including the Elwha River east to the Dunge—
ness River (Figure VI—16) (Williams et al. 1975). Probable use
by the coho is suspected to occur in Tumwater, Lee’s and Bagley
Creeks (Figure VI-16) (Williams et al. 1975). Coho salmon use
in Valley and Peabody Creeks is believed to be extinct (Wil-
liams et al. 1975). Major runs occur in the main stem and
access tributaries of the Elwha and Dungeness Rivers and in the
accessible length of Morse, Siebert and McDonald Creeks (Wil-
liams et al. 1975).
In the Elwha - Dungeness Basin, coho spawning migrations are
usually later than in other Puget Sound drainages (Williams et
al. 1975). Upstream migrations in the Elwha and Dungeness Rivers
usually begin in mid-September and continue until mid-December
(Table VI-25). The runs in the independent tributaries begin
later following fall and winter rains which increase the flows
332

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in the creeks (Williams et al. 1975). Spawning is initiated
in mid-November and the fry begin to emerge in March. These
juveniles usually remain in the tributary until the following
spring before migrating to salt water. High populations,
low water and availability of food force some juveniles to
migrate to the lower river during the sununer or fall following
emergence (Williams et al. 1975).
Utilizing coho populations in the Strait, salmon spawning
ground counts and other census data, the WDF estimated relative
natural escapement for coho entering the Elwha and
Dungeness Rivers, and Morse, Siebert and McDonald Creeks
(Table VI-J-2) (ziligis personal communication of November 12,
1980).
From 1976 to 1979 the Elwha Hatchery averaged a return of 803
fish/year; whereas the Dungeness Hatchery (1965 — 1979) averaged
6167 fish/year. In 1978 a total of 2,113,197 fry (0 to 14 days
reared), fingerlings (15 to 269 days reared) and yearlings were
reared in the Elwha Hatchery and planted in the Elwha or Dunge-
ness Rivers (Table VI-J-3). During 1977 the Dungeness Hatchery
planted a total of 674,206 coho in Morse, Siebert, and McDonald
Creeks and the Dungeness River (Table VI—J—4).. In 1978 1,417,900
fingerling and 868,366 yearlings were planted by the Dungeness
Hatchery into independent tributaries of the study area (Table
VI-J-4). Fresh water sport catch totaled 156 fish and 6700 fish
in the Elwha and Dungeness Rivers, respectively (Table VI-J—5).
Chum Salmon: The Elwha River supports a major run of chum
salmon and a minor run occurs in the Dungeness River (Williams
et al. 1975). Limited chum salmon use occurs in Ennis, Morse,
Siebert, and McDonald Creeks (Williams et al. 1975). The WDF
speculates probable use also occurs in Dry, Tumwater, Valley,
Lees, and Bag].ey Creeks (Figure VI-16). The Elwha - Dungeness
basin supports a separate early (September) and late (November)
333

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chum run. The early run occurs in the Dungeness River and the
late run in the Elwha River and Ennis, Morse, Siebert and Mc-
Donald Creeks (Williams et a].. 1975). A very limited (less
than 100 fish) late run is also believed to exist in the Dunge—
ness River (Williams et a].. 1975).
During the early run chum spawn from late September to early
October (Table VI—25). In the Elwha River and other indepen-
dent tributaries, spawning does not begin until late November
and continues through December (Table VI-25). The juvenile chum
usually remain in the fresh water system 2 to 3 months and com-
plete their major downstream migration by mid-June (Table VI-25).
During WDF salmon spawning ground counts chum were observed
in the Elwha and Dungeness Rivers and Morse Creek (Table VI-J-1).
Additional chum census was not conducted by WDF on the Elwha and
Dungeness Rivers; therefore annual natural escapements are not
available (Ames, personal communication of November 12, 1980).
Chum salmon are not spawned in either of the two hatcheries in
the study area; therefore, there is no artificial escapement
for this species.
Pink Salmon: During odd numbered years both the Elwha and
Dungeness rivers support major runs of pink salmon (Williams
et al. 1975). Morse Creek has a minor pink salmon run and Mc-
Donald Creek is known to support a limited number of this spec-
ies (Williams et al. 1975). The Dungeness River supports 2
distinct runs of pink salmon; however, only one run exists in
the Elwha River and Morse Creek (Williams et al. 1975).
The earliest salmon spawning migration of all Puget Sound rivers
occurs in the Dungeness River (Willaims et al. 1975). The
early run begins upstream migration in July and spawns during
late August to early September in the upper (above river mile
10.0 (16.1 1cm)) Dungeness River and Gray Wolf River (Table VI—25).
334

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The late run begins in late August and continues through mid-
September. Most of these adults mature and spawn in the lower
4 miles (6.4 kin) of the Dungeness River. Spawning usually
occurs from September 15 to October 20 (Williams et al. 1975).
In the Elwha River the adult run occurs from late August to
September (Table VI-25). The fish spawn during late August
through October. Spawning is confined to those suitable gravel
areas below the lower Elwha Dam located at river mile 3.4
(Williams et al. 1975). The run in Morse Creek occurs in the
lower 2 miles. Spawning by this species occurs from late
September through mid-October (Williams et al. 1975). Down-
stream juvenile migration in all these tributaries is complete
by mid-June (Table VI-25).
Utilizing hatchery rack counts and salmon spawning ground data,
a natural escapement average of 10,170 pinks/year and 85,740
pinks/year return to the Elwha and Dungeness rivers, respective-
ly (Table VI-J—2). The artificial escapement for the Dungeriess
Hatchery averaged (1975, 1977, 1979) 23,967 pinks/year (Table VI—
J-3). In 1978, 302,400 fingerlings were planted by this hatchery
in the Dungeness River (Table VI-J-4). Sport catch for pinks
in the area was only reported for the Dungeness River in 1975.
This totaled 125 fish (Table VI—J—5).
Steelhead Trout: Stee].head trout utilize all the accessible
tributaries in the study area (Figure VI-16) (PNRBC 1970).
As a game fish the steel head trout can only be harvested for
sport with the exception of treaty Indian tribes that may
harvest the species commercially. Steelhead punch cards re-
trieved from anglers (1962 - 1978) and reported treaty Indian
catches (1975 — 1978) provide the WDG an estimated steelhead
return for the E].wha River, Morse, Siebert and McDonald Creeks
and the Dungeness River (Table VI-J-6).
During May, summer steelhead begin upstream migrations into the
tributaries of the study area (Table VI—25). The migration is
335

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complete by mid-October. Spawning occurs early the following
spring (mid-February ) (Withler 1966). Intragravel develop-
ment is complete by mid-July. The fry remain in the fresh-
water system 1 - 4 years before migrating downstream in April
and May (Withler 1966).
Winter steelhead begin their migrations into the tributaries
of Port Angeles in early December (Table VI-25). Fry emergence
is complete by August. These juvenile fish remain in the
streams for 1 — 4 years followed by a downstream migration in
mid—March (Withier 1966).
The Elwha and Dungeness Rivers support the largest winter and
summer steelhead runs in the study area (Table VI-J—6). Small
migrations (2 — 334 fish) of winter stee].head also utilize Morse,
Siebert and McDonald Creeks (Table VI-J-6).
Searun Cutthroat and Doily Varden Trout: All the accessible
independent tributaries in the study area are utilized by searun
cutthroat (PNRBC 1970). The tributaries to the rivers and
independent drainages are the principal spawning areas; how-
ever the mainstems of the these fresh water systems are the
major rearing grounds (PNRBC 1970).
In the Port Angeles tributaries, searun cutthroat begin migrat-
ing upstream in late May (Table VI—25).. Spawning is complete by
early April. After the fry emerge in June they remain in the
system for 1 - 3 years before migrating downstream (March —
June) (Scott and Crossinan 1973).
Anadromous Dolly Varden trout are known to occur in large
tributaries that have deep pools adjacent to shallow gravel
areas ( 1wha and Dungeness River) (PNRBC 1970). Fresh water
life cycles for this species are not available for the study
area.
336

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C. Population and Die tributi .on of Anadromous Fiah in Marine
Watera Adjacent to Port Angeles Harbor
Downstream migration of juvenile anadromous species occurs
during high river flow (March - July) (PNRBC 1970). Upon
entering the brackish (having less salt than seawater) coastal
waters, 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 chi-
nook enter the brackish waters as small fry and usually remain
nearshore for a longer period of time than species migrating
as smolts (coho, sockeye, spring chinook and steelhead) (USD1
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).
A study of the occurrence of juvenile salmon in the Harbor was
conducted in the spring of 1964 (USD1 1967). The beach seines
revealed high concentrations of juvenile pink and chum salmon
in the Harbor (Table VI-26). The highest concentrations occurred
along the eastern portion inside Ediz Hook (Stations A and C).
Beach seine hauls conducted by ITT Rayonier personnel for both
marine and anadromous species revealed chinook, chum and coastal
cutthroat species occurred immediately east of ITT Rayonier to
Morse Creek (Table VI-27). Beach seines conducted during July
1962 revealed the highest concentration of chinook and chum
salmon (Table VI-27).
In addition to juvenile salmon surveys the WDF estimated the
quantity of adult salmon species commercially harvested with
all net gear in the marine waters of the study area. Catch data
is tabulated according to commercial reporting areas (Figure vi—
17). The marine sport catch reporting areas in the vicinity of
Port Angeles extend from Low Point east to Admiralty Inlet;
therefore, WDF sport data is not available specific to the study
area. -
337

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Table VI-26. NUMBERS OF JUVENILE SALMON CAUGHT OR SEEN IN PORT
ANGELES HARBOR, APRIL - MAY 1964
Source: USD1 1967
(Refer to Figure VI-H-2)
Station
Species
Total Number
Caught by
Beach Seining
Estimated Number
Visually
Observed
A
Pink and Chum
Chinook
Silver
419
2
1
50
B
Pink and Chum
2
C
Pink and Chum
349
1,100
D
Pink and Chum
78
1
E
Pink and Chum
Searun Cutthroat
205
4
Boat Basin
Pink and Chum
35
338

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Table VI-27. ANADROMOUS SPECIES COMPOSITION OF THE PORT ANGELES AND DUNGENESS SEINE HAULS
Source: Stein and Denison 1966
(Refer to Figure VI-H—1)
Port
Angeles Harbor
Dungeness*
1961
1962
1964
1965
1966
Grand
1965
Species
Oct.
12
July
11
Sept.
3
6/29-8/2
July
12
Total
Coastal Cutthroat
2
6
7
7
22
2
Chinook Salmon
81
5
4
1
91
9
(juvenile)
Chum Salmon
24
24
(juvenile)
Pink (juvenile)
Total
1
2
111
12
11
1
147
12
* No station location available

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12?3O
123”20’
121 1Ol
12J’OO’
Figure VI-li. COMMERCIAL SALMON HARVEST AREA DESIGNATED BY WDF
STRAIT OF JUAN DE FUCA
0
15 3 45 6
DE.S%GtU IE 6D
—
mUss
4.1s Harbor
I Protsctlon
L .\

-------
Previous to 1980 commercial catch data from Dungeness east to
Admiralty Inlet was also incorporated into the Port Angeles catch.
In 1979 the Harbor was designated as a separate catch reporting
area (6D) by WDF (Figure VI—17). As a result the commercial data
for the study area is first available for the year of 1980
(estimate as of November 1980)
Species Estimated Catch
Chinook 35
Coho 5369
Chum 93
An analysis of the freshwater artificial salmon escapements,
salmon plantings, fresh water sport catch and commercial catch
indicates coho populations are the largest utilizing the study
area (Tables VI-J—3, VI-J—4, VI—J-5).
d. Marine Fish Occurrence and Distribution
During the six year period from 1961 to 1966, 27 marine fish
species were seined from 12 nearshore locations east of ITT
Rayonier (Figure VI-H—l, Table VI-28) (Stein and Denison 1966).
English sole, Pacific herring, surf smelt and snake prickle-
back were the predominant species for the five year sample
period (Table VI-K-].). According to findings of the most re-
cent surveys and studies (1973 — 1978), an additional 34 demer-
sal or neritic marine species occur in the Port Angeles area
(Tables VI-28, VI —K-].) (WDF unpublished data 1973 — 1978; MSN
1977; Sixnenstad et al. 1977; unpublished NOAA—MESA data for
Cross et al. 1978). Based on the 1977 — 1978 nearshore abun-
dance data (number of fish) collected at Morse Creek and Dun—
geness Spit (Cross et al. 1978), eight species dominated the
nearshore waters (beach seine, townet) and two species were
predominant in the intertidal areas (tidepool collection)
(Tables VI—29, VI—K—2)
In analyzing the results from all sampled locations (Figure VI-H
3) (1976 — 1978) in the Strait, the authors (Cross et al. 1978)
determined dominant species according to occurrence (species/
sample), density (species/area, species/volume or species/rock)
341

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Table VI-28. MARINE SPECIES OCCURRING IN THE PORT ANGELES AREA(a)
Common Name Scientific Name Reference
Northern anchovy E’ngraulis mordax 1,2
Cabezon Scorpaenichthys marmoratue 1
Northern clingfish G’obiesox maeandricus 2
High cockscomb Anopiarchu8 purpurescens 2
Pacific cod Gadus maorocepha us 4
Spiny dogfish Squa lie acanthias 2
Starry flounder Platichthye ate ilatue 1,2
Crescent gunnel Pholie lacta 1,2
Kelp green].ing 1fexagrc ivnos decagraminus 2
White—spotted greenhing Hexagrcwrmos ate Zleri 1
Penpoint gunnel Apodichth!Js flavidue 2
Saddleback gunnel Pholia ornata 1,2
Pacific halibut Hippogloasus steno lepis 3
Pacific herring Clupea hai’engua pallassii 1,2
Lingcod Ophidon elongatus 1,4
Shiner perch Cymatogaater aggregata 1,2
Striped perch Embiotoca lateralie 1,2
Bay pipefish Syngnathus griseolinatus 2
Sturgeon poacher Agonus acipenserinua 1
Tubenose poacher Pallasina barba a 1,2
Warty poacher Occella verrucoaa 2
Walleye pollock Theragra chalogr ivna 1,2
Black prickleback Xiphister atropurpureus 2
Rock prickleback Xi phi ater mucoaus 2
Ribbon prickleback Ph tichthya chiras 2
Snake prickleback Ew7rpenua sagitta 1,2
Ratfish Hydrolagus colliei 2
Chinook salmon* Onchorhynchus techc ytscha 1,2
Chum salmon* onchorhynchus keta 1,2
Coho salmon* cmohorhynchue kisutch 2
Pacific sanddab Citharichthye etigmaeus 2
Speckled sanddab Cithariohthya sordidue 1,2
Pacific sandlance Anvnodytes hexapterus 1,2
Buffalo sculpin Enophrya bison 1,2
Calico sculpin Clinocottue embrym 2
Darter sculpin Rathhlinus boleoidea 2
Fluffy sculpin Oligocuttus enyd ri 2
Grunt sculpin Rh nphocottus richardeoni 2
Manacled sculpin Synchirus gilli 2
Mosshead sculpin Clinocottue globicepa 2
Padded sculpin Artedius fenestralis 1,2
Pacific staghorn sculpin Leptococcus armatus 1,2
Rosylip sculpin Aacelichthys rhodoras 2
Saddleback sculpin oligocottus rimensis 2
Sharpnose sculpin Clinocottue acuticeps 1,2
Silverspotted sculpin Blepsias cirrhosua 2
Smoothhead sculpin Artedius lateralis 2
Soft sculpin G ibertidia aigalutea 2
Tadpole sculpin Peychrolutea paradoxus 2
342

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Table VI—28. page 2
Common Name
Scientific Name
Reference
Tidepool scu].pin
Olig000ttuB rnaculosue
1,2
Long fin smelt
Spirinchus thaleighthys
2
Surf smelt
Ringtail snailfish
Hypomeau8 pretiosus
Liparis rutteri
1,2
2
Showy snailfish
Liparis puichellus
2
Tidepool snailfish
Liparis florae
2
C—O sole
Pleuronic hthye coenosus
2
Dover sole
Microetwnus pacificuB
3
English sole
Parophrys vetulu8
1,2,4
Rock sole
Lepidopsetta bilineata
4
Sand sole
P8ett7 .chth /8 melanoeticus
1,2
Three—spined stickleback
Gasterosteus acuZ eatus
1,2
Pacific tomcod
Cutthroat trout*
tficrogadus piioximus
Salmo clarki
1,2
1
Tubes flout
Aulorhynohus flavidus
2
Turbot
Artheresthes stomias
4
* The text does not total these sampled anadromous fish with
marine species.
Reference Key: 1 Stein and Denison 1966
2 unpublished NOAA-MESA data for Cross et al. 1978
report
3 WDF unpublished data 1973 - 1978
4 MSN 1977
(a) Occurrence data collected in 1976 (Simenstad et al. 1977) is
very similar to the 1977 — 1978 data (Cross eEaIT 1978) and
is therefore not referenced separately from o i et a].. 1978.
343

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Table VI-29. DOMINANT NEARSHORE MARINE SPECIES SAMPLED FROM
MORSE CREEK AND/OR DUNGENESS SPIT, 1977, 1978*
(Refer to Table VI-K—1)
Common Name
Genera Species
Collection
Type
High cockscomb
Anoplarchus pur’purescefls
T
Pacific herring
Clupea harengus
B, Tn
Shiner perch
Cymatogc.ater aggregata
B
Pacific sandlance
Ammodytes hexcrpterus
Tn
Tadpole sculpin
Peychorlutes paradoxus
Tn
Tidepool sculpin
Oligocottus maculosus
T
Surf smelt
Hypomeaus pretio8ua
B, Tn
English sole
Par phryB vetulus
B
Sand sole
Psettichthye melanosticus
B
Pacific tomcod
Microgadus proximus
B
* An average of forty fish or more/area sampled (beach seine and
townet) or two fish or more/area sampled (tidepool) represents
a dominant species.
Collection Key: B - Beach seine
Tn- Townet
T - Tidepool
344

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and biomass (total organic wet weight). Utilizing this data,
Pacific staghorn sculpin, English sole and sand sole are the
most abundant and widely distributed nearshore marine fish
seined along the Southern Strait (Cross et al. 1978). Pacific
herring (larvae and juveniles) dominate the neritic biome
(townet samples) in the Strait. Larval herring predominate
in the spring and juveniles are abundant throughout the remain-
der of the year. During 1977 - 1978 the greatest herring catch
occurred at Morse Creek and Beckett Point. Longfin smelt is
the next most abundant townet species of the Strait. This
species did not dominate the Port Angeles area; however 99
percent of the longfin smelt were collected at Twin Rivers and
Pillar Point. Pacific sand lance (larvae) also occur in abun-
dant quantities during the spring along the eastern Strait.
Intertidal species of tidepool sculpin, high cockscomb, and
northern clingfish are found along the southern shores of the
Strait. These species tend to be concentrated along cobble
beaches such as Morse Creek.
High densities (number of fish/rn 2 - beach seine, number of
fish/rn 3 — townet, number of fish/rock - tidepool) of demersal
species occur during the summer along exposed sites (Dungeness
Spit) resulting from large schools of herring and sand lance
(Cross et a].. 1978). Neritic species are the most dense dur-
ing the spring and summer along most of the Strait (Cross et al.
1978). The increased spring density is attributed to abundance
of larval species (Pacific herring and sand lance). Morse
Creek (moderately exposed) had highest densities during 1977 -
1978 which contradicts findings of 1976 - 1977 in which high-
est densities occurred in eelgrass beds (Cross et a].. 1978).
Along the Strait densities of intertidal fish species are maxi-
mum during late summer and early fall (Cross et al. 1978).
Utilizing available interview data, the WDF estimates the conun-
ercial bottomfish trawl catch in designated marine waters of
Puget Sound and the Strait. According to the commercial catch
345

-------
data, waters immediately east of the Harbor and on the north
side of Ediz Hook support a significant commercial bottom
fisheries (WDF, unpublished data 1973 — 1979; DNR 1977) (Table
VI—30). Pacific true cod, rockfish species and the spiny dog-
fish shark are the major commercial species in the area. Bottom
fish sport catch estimates are not available specifically for
the Port Angeles area.
Critical habitat areas are designated for two fish species in
the study area (Figure VI-18). Pacific halibut, a f].atfish
occurs in sand and mixed-fine type bottoms. This species occurs
in waters 12 to 13 fathoms and deeper off Ediz Hook, Green Point
and Dungeness Spit (MSN 1977). A small spawning stock of surf
smelt utilize Dungeness Bay (MSN 1977; DOE 1978).
F. WILDLIFE
Various classes of wildlife can be found in the study area in
Port Angeles Harbor and at other locations between the Elwha
and Dungeness Rivers. The most abundant wildlife group poten-
tially affected by pulp mill effluents are marine birds; how-
ever, marine mammals are also present, though in smaller numbers.
The main attraction for pinniped mammals (seals) and marine
birds is the area surrounding Dungeness Spit which is desig-
nated as the Dungeness National Wildlife Refuge, administered
by the U.S. Fish and Wildlife Service. Cetacean mammals (whales)
are more generally distributed throughout the study area.
The effects of pulp mill effluents or related toxic compounds
on marine birds or mammals have not been studied. Since these
are both air breathing organisms, it is unlikely that direct
physiological effects on the organism are significant. Trans—
ference of toxic compounds through the food chain, or altered
food resources are the most likely source of effects (see Chap-
ter VII). In the subsections below are documented the organisms
346

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Table VI-30. TOTAL ESTIMATED POUNDS OF THE COMMERCIAL BOTTOMFISH
TRAWL CATCH IN THE PORT ANGELES AREA
Source: WDF, unpublished data 1973 - 197.8
Species
1973
1974
1975
1976
1977
1978
Pacific true
cod
28,888
932
7172
9943*
23,590
N/C
Lingeod
812
N/R
1807
N/R
N/R
N/R
Rockfish
16,081
218
1866
4629
4248
7871
Spiny dogfish
shark
N/R
N/R
N/R
3009
17,829
94,680
Dover sole
N/R
1180
N/R
N/R
4163
891
English sole
403
N/R
443
353*
1107
4481
Petrale sole
107
N/R
20
N/C
67
258
Rock sole
N/R
N/R
N/R
N/R
450
56
Turbot
N/R
N/R
N/R
N/R
N/R
288
* Includes bottomfish catch from the Dungeness area and Port Angeles area
N/R — no commercial catch reported
N/C - data not complete

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Figure VI-18. CRITICAL
HABITAT
AREAS
IN
THE PORT ANGELES AREA
Source:
MSN 1977; DOE
1978
I2 f3O
12
•P.cφflc
Halibut
STRAIT OF JUAN DE FUCA
12010’ - 12 OO’
1 1 5
123w

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known to be present in the area and, where data exists, known
abundances or densities.
1. Marine Mammals
The Marine Mammal Protection Act, passed in 1972, initiated
extensive research on marine mammals in the United States.
Prior to this, commercia]. and treaty regulated species were
the main marine mammals under study. As a result, extensive
studies in this mammalian field are limited.
Studies and Methods: There are presently three available
published studies describing the current distribution of mar-
ine mammals in the Strait. These were conducted by Mathemati-
cal Sciences Northwest, Inc. (MSN), Northern Tier Pipeline Co.
(NTPC), and the National Oceanic and Atmospheric Administration
(NOAA).
From 1974 — 1977 a Marine Baseline Study of Northern Puget
Sound was conducted by the DOE. MSN (1977) was contracted by
DOE to inventory present fauna species and determine their
life history, distribution and habitat requirements. Critical
habitat areas were summarized from the resulting data.
NTPC (1979) conducted marine mammal surveys of Port Angeles
Harbor and the shoreline east to Dungeness Spit. Boat tran-
sects within the Harbor and both nearshore and offshore waters
east to Dungeness Spit were conducted from February 15 — May
8, 1978. Species composition and abundance were recorded for
species occurring within 300 yards on each side of the tran-
sect. In addition to field observations, NTPC also included
additional information on existing mammalian literature and
observations.
A study describing the distribution and abundance of marine
mammals in the Strait and Northern Puget Sound was initiated
349

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by NOAA in November 1977 (Everitt et al. 1979). The first
year t s work of the two year program (November 1977 - October
1978) involved aerial, small boat, and land observations of
seals and otters. Additional publications were used to des-
cribe those species which were not observed during these
field observations. The majority of cetological (whale) data
were obtained from observations made by the Moclips Cetalogi-
cal Society ORCA Survey, the Whale Hot].ine and the Platforms
of Opportunity Program (POP). The POP is a computed data bank
of whale sitings reported to the Marine Mammal Division of NOAA.
Review of Individual Mammal Survey8: MSN identified five
common species in the Strait. Critical habitat areas for
only two of these species (Harbor seal and River otter) were
identified in the Dungeness Bay area (Figure VI—19), The nor-
thern sea lion has designated critical habitat areas on rocky
islands near but outside the study area. Data is generally in-
sufficient to identify potential critical areas for the killer
whale and the Pacific harbor porpoise.
The NTPC field studies resulted in observations of only three
marine mammal species in the Port Angeles area. These included
the harbor seal, northern sea lion and gray whale. The first
two are considered common to the Strait; however, the gray
whale is presently considered an endangered species by the
federal government.
Using existing data, NTPC identified twenty marine mammal
species in the Port Angeles area (Table VI-31). Eight of these
are considered to be common and seven occur occasionally in
the Strait (Table VI-32, VI-33). Others are found infrequently.
During the NOAA study (Everitt et al. 1979), nine marine
mammal species were identified in the Port Angeles area. These
are shown in Table VI-3l. Detailed field data was collected
350

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12 r30’
12120’ 12i’lO’
12i’0O’
-J-
Figuze
VI-19. CRITICAL MARINE MAMMAL AREAS
Source:
MSN 1977
-Rlvsr tsr
___ STRAIT OF JUAN DE FUCA
48’lo’
mUss
I Ang.f.s Harbor
I T T
Protsct lon
L!.\
I

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Table VI-3].. MARINE MAMMALS IN THE VICINITY OF PORT ANGELES
Source: NTPC 1979
California Sea Lion
Dali Porpoise
Fin Whale
False Killer Whale**
Goosebeak Whale**
Gray Whale
Harbor Porpoise
Harbor Seal
Humpback Whale
Killer Whale
Minke Whale
Northern Elephant Seal
Northern Fur Seal
Northern Sea Lion
Northern Pacific Giant Bottlenose
Whale* *
Scientific Name
Zalophus californjanus
Phocoenojdes dalli*
Balaenoptera physalus
Pseudorca crassidens
Ziphius cavirostris
Eschrichtjus robustus*
Phocoena phocoena*
Phoca vitulina*
Megaptera ncvaeangliae
Orcinus orca*
Balaenoptera acutoros trata
Mirouga angustirostris*
Callorhinus ursinus
Eumetropias jubata
Berardius bairdii*
Common Name
Northern Pacific Whiteside Dolphin Lagenorhynchus obliguidens
River Otter Lutra canadensis*
Saddleback Dolphin** Deiphinus delphis
Shortf in Pilot Whale** Globicephala macrorhynchus*
Sperm Whale Physeter macrocephalus
* , eported by Everitt et a].. (1979) and NTPC (1978)
**These species have been documented by only one record in the
Strait of Juan de Fuca or other inner waters.
352

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Table VI-32. COMMON MARINE MAMMAL SPECIES IN THE
STRAIT OF JUAN DE FUCA
Common Name Scientific Name
California Sea lion Zalophus caiifornianus
Dali porpoise Phocoenoides dalli
Harbor porpoise Phocoena phocoeha
Harbor seal Phoca vituiina
Killer whale Orcinus orca
Minke whale Ba].aenoptera acutorostrata
Northern sea lion Eumetropias jubatu
River otter Lutra canadensis
Table VI-33. OCCASIONAL MARINE MAMMAL SPECIES IN THE
STRAIT OF JUAN DE FUCA
Common Name Scientific Name
Fin whale Baiaenoptera physalus
Gray whale Eschrichtius robustus
Humpback whale Megaptera novaeangliae
Northern elephant seal Mirouga angustirostris
Northern fur seal Callorhinus ursinus
Northern Pacific white—side dolphin Lagenorhynchus oblig uidens
353

-------
Only on harbor seal observations. This information is con-
tained in Table VI-34 for Low Point (immediately west of the
study area) as well as Green Point and Dungeness. Whale move-
ments have also been reported by Everitt et al. (1979), and
although high usage areas have not been determined, it is
known that Puget Sound’s largest killer whale pod (L pod)
migrates at times along the southern shoreline of the Strait
(Figure VI-20). This pod is thought to contain roughly 45
whales.
2. Marine Birds
The principal attraction for marine birds in the study area is
the Dungeness Spit area, including the offshore waters of the
Strait and the sheltered waters of Dungeness Bay, as well as
Dungeness Spit itself (Figure VI-21). The spit and portions of
adjacent marine waters constitute the Dungeness National Wild-
life Refuge. Port Angeles provides a less attractive marine
bird habitat due to shoreline development in Port Angeles and
Ediz Hook and possibly due to effects on water quality of in-
dustrial effluents. Observations of marine birds in low to
moderate numbers have been made, however, both inside the Har-
bor and outside Ediz Hook as well as at various points between
Port Angeles and Dungeness Spit (Tables VI-35 and VI-36).
A list of marine bird species observed at several locations
in the study area has been prepared from various sources
(Table VI—35). No comprehensive quantitative studies are known
to have been made for the study area, although Manual et al.
(1979) has projected total populations from point observations,
aerial overflights and other methods. These estimates show
that roughly 70 marbled murrelets and 130 pigeon guillemots
use the waters immediately west of Ediz Hook with between
100 — 150 of each species utilizing Dungeness Spit and Bay,
with only a few of these birds in or near Port Angeles Harbor.
354

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Table VI-34. HARBOR SEAL ABUNDANCE IN AND NEAR THE STUDY AREA
Source: Everitt et al. (1979)
Date Dungeness Refuge Green Point Low Point
11/30/77 0 0 45
12/8/77 0
12/21/77 0 0 1
1/26/78 59
1/28/78 69 0 8
2/9/78 1 8
2/24/78 70
2/28/78 18 0 6
3/14/78 50
3/15/78 34 0 3
4/25/78 9
4/28/78 81 0 0
5/23/78 10 0 1
5/25/78 35
6/9/78 41
6/27/78 20
6/28/78 26 1 1
7/4/78 45
7/19/78 40 2
7/20/78 41 1 1
7/27/78 33
8/18/78 30 0
8/29/78 54 2 38
9/12/78 8 2 33
10/14/78 43
10/31/78 66 3 0
-
355

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Figure VI-20. MOVEMENTS OF “J” AND “L” PODS OF KILLER
WHALES IN PUGET SOUND AND THE STRAIT OF
JUAN DE FUCA
Source: Everitt et al. 1979
356
0 PORT*I GELES

-------
DUNGENESS BAY
r t
Figure VI-21.
DUNGENESS BAY AND THE ASSOCIATED DUNGENESS NATIONAL WILDLIFE
REFUGE BOUNDARIES
/,o
C
)

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Table VI-35. OCCURRENCE OF MARINE BIRDS AT PORT ANGELES HARBOR
AND VICINITY
Source: Salo 1975 (1) ; Canning 1976 — 1979 (2)
Strait of
Juan de
Port
Angeles
Dungeness
Spit and
Species Fuca
Harbor Ediz
Hook vicinity
Common Loon 1 1,2
Artic Loon 1 1
Red-throated Loon 1 1,2
Red—necked Grebe 1 1,2
Horned Grebe 1 1,2
Eared Grebe 1 1,2
Western Grebe 2 1,2 1,2
Double—crested 1 1,2
Cormorant
Brandt’s Cormorant 1 1 1
Pelagic Cormorant 2 1,2 1
Great Blue Heron 1 1
Canada Goose 1 1
Black Brant 1 1
White-fronted Goose 1
Snow Goose 1
Mallard 1 1,2
Pintail. 1 1
Green—winged Teal 2
American Wigeon 1 1,2
Shoveler 1
Canvas back 1
Greater Scaup 1 1
Lesser Scaup 1 1
Corrunon Goldeneye 1 2 1
Barrows Goldeneye 1 1,2
Bufflehead 1 1,2
O ldsquaw 1,2 1,2
Harlequin Duck 1 1
White—winged 2 1,2 1,2
S Co ter
358

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Table VI—35. Continued, page 2
Strait of
Juan de
Port
Angeles
Dungeness
Spit and
Species Fuca
Harbor Ediz
Hook vicinity
Surf Scoter 1,2 1,2 1,2
Black Scoter 1 1.
Hooded Merganser 2 2
Common Merganser 1 1
Red-breasted 1 1,2
Merganser
Bald Eagle 1.
American Coot 1 1
Semi-palinated Plover 1
Ki lldeer 1 1,2
Black-bellied Plover 1 1,2
Ruddy Turnstone 1 1
Black Turnstone 1 1
Whimbrel 1 1
Spotted Sandpiper 1 1
Wandering Tattler 1
Greater Yellowlegs 1 1
Knot 1
Least Sandpiper 3. 1
Dunlin 1 1
Dowitcher 1
Sanderling 1 1
Western Sandpiper 1 1
Wilson’s phalarope 1
Glaucous—winged Gull 2 1,2
Western Gull 1 1
Herring Gull 1
Thayer’s Gull 1 1
California Gull 1 1
Ring-billed Gull 1 1
Mew Gull 1,2 2 1
359

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Table VI-35. Continued, page 3
Species
Strai
Juan
Fuca
t of
de
Port Angeles
Harbor
Ediz
Hook
Dungeness
Spit arid
vicinity
Heermann’s Gull
].
1
Bonaparte’s Gull
1
1
Common Tern
1
1
Common Murre
1
1
Pigeon Guillernot
1
1
Marbled Murrelet
1
1
Rhinoceros Auklet
1
1
Belted Kingfisher
1
1,2
360

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Table Vt-36. PEAK CONCENTRATIONS AND SEASON OF SELECTED MARINE
BIRDS IN INNER STRAIT OF JUAN DE FUCA
Source: Derived from Manuwal et al. 1979
Shearwaters
Storm—Petrals
Cormorants
Herons
Ducks and Geese
Oyster Catchers
Plovers
Sandpipers and
Shorebirds
Phal aropes
Jaegers
Gulls and Terns
Alcids
Eagles and Hawks
80 F
80 S
1900 W
40 F
8000 W
10 Sp
30 S
30 F
880 F
10 F
1 all
1 Sp,F
4 Sp,W
is
1 F,W
1 all
2F
170 W
2F
1600 W
3F
4F
60 F
290 F
2900 W
2S
850 F
300 F
210 F
30 S
5800 W
4S
560 F
1200 Sp,W
Loons
Grebes
Inner
Ediz
Port
Green
Dungeness
Dungeness
Strait
Hook
Angeles
Point
Spit
Bay
(301)
(302)
(303)
(304)
(305)
(306)
660 W
6660 F
1 Sp,F,W
2 Sp,W
60W
290 W
30 F
70 F
50W
230 Sp
iF
9W
240 W
130 F
low
600 W
20W
110 W
2200 F
50W
680
470
3,000
1,700
Spring Total
Summer Total
Fall Total
Winter Total
34,000 W
28,000 F
14,000
7,800
67,000
66,000
20 F
7F
1W
10
10
30
10
2500 F
670 Sp
3F
3,100
4,000
4,600
3,800
2700 F
280 F
640
2,000
4,800
3,600
iF
3500 F
140 Sp
6,100
2,900
7,200
8,800

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anuwal’s data have also been u.sed to summarize seasonal
maxima within various bird groups (Table VI-36).. Due to its
large shoreline area, the Inner Strait west of Port Angeles
supports the highest numbers of such birds as grebes, cor—
morants, waterfowl (duck and geese), gulls and alcids. If
the small areas constituting Dungeness Spit and Bay are com-
bined, however, it is clear that this area holds high densi-
ties of waterfowl, shorebirds, heron, plovers and others.
Even Green Point supports important concentrations of winter-
ing waterfowl.
Seasonal abundance of shorebirds and waterfowl is generally
greatest in the fall and winter. Bird counts are generally
taken during the period November - February (Table VI-37)
At Dungeness, most species abundances seem to peak in December
or possibly January. Annual winter waterfowl counts are taken
by the U.S. Fish and Wildlife Service in early January each
year. Comparison of counts in several recent years shows
a general decreasing trend (Table VI—38).
Most marine birds in the study area feed on either submerged
grasses found in the bays or creek mouths, or on small benthic
organisms or fish in the intertidal and shallow subtidal zones.
At the creek mouths, such as Morse Creek, there are generally
beds of algae and seagrasses, with accompanying benthic com-
munities utilized by shorebirds. The Dungeness River contains
both submerged plants, marsh plants (used for both food and
shelter), and a fairly diverse benthic population (Cross 1978;
Nyblade 1978).
Both waterfowl and shorebirds are migratory. While some resi-
dents of various species remain year round, numbers fluctuate
rapidly during migration seasons. It is clear from the data
in the tables shown in this section that the Harbor, Strait
shoreline and Dungeness River support large densities of birds
362

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Table VI-37. U.S. FISH AND WILDLIFE COUNTS IN PORT ANGELES AREA 9 1978
Source: U.S. FWS unpublished data 1978 - 1979
Pillar Pt. to
Species Port Angeles
Port Angeles
to Dungeness
Dungeness
Area
and NWR*
2/79 Sequim Bay
11/78
12/78
Western Grebe 46 192 128 65 393 0
Canada Goose 0 0 0 0 0 0
Black Brant 0 0 109 86 74 1
Mallard 0 0 1225 2110 685 70
Gadwall 0 0 45 0 0 18
Pintail 45 0 659 195 23 22
Green Wing Teal 0 0 715 290 50 187
Widgeon 78 76 6405 6114 812 488
Shoveler 0 0 0 0 0 0
Redhead 0 0 0 0 0 40
Canvasback 0 0 25 0 0 0
Greater Scaup 115 6 150 256 125 72
Goldeneye 0 53 270 422 200 3
Bufflehead 190 70 460 1356 695 86
O ldsquaw 6 25 0 80 7 0
Scoter 145 207 387 404 480 278
Merganser 35 25 125 68 84 10
Coot 0 0 0 20 0 0
Loon 6 1 10 15 0
* National Wildlife Refuge

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Table vi-38. WATERFOWL OBSERVED IN CALALLAM CO. BY U.S. FISH AND
WILDLIFE SERVICE 1975 — 1979 (Includes Lake Crescent
and Other Freshwater Areas as Well as Marine Waters)
Source: U.S. FWS
Waterfowl 1975 1977 1978 1979
Mallard 3,701 10,400 2,115 3,301
Gadwal]. 170 -— —— ——
Widgeon 1,426 19,481 10,974 4,045
Green Wing Teal 532 70 1,715 235
Blue Wing Teal 0 0 0 14
Cinnamon Teal 0
Shoveler 12 0 31 96
Pintail 1,874 210 2,201 333
Wood Duck 0 - — —— ——
Total Dabblers 7,715 30,161 17,036 8,024
Redhead 0 0 0
Canvasback
Scaup 1,224 2,650 1,804 779
Ring-necked - - -— -- --
Goldeneye 1,015 815 497 268
Bufflehead 1,829 1,750 1,341 1,836
Ruddy Duck 257 1,430 585 140
Total Diving Ducks 4,325 6,645 4,226 3,035
Scoter 7,091 0 2,960 1,265
Oldsquaw 44 0 0 110
Harlequin 2 0 80 0
Merganser 14 0 114 145
Unid 978 -— ——
Canada Goose 112 320 0 171
Brant 518 455 504 135
Swans 4 —— -— ——
Total Waterfowl 21,067 37,581 24,921 12,885
364

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at certain times of year. Dabbling ducks depend directly
on primary productivity of algae and seagrasses, while
diving ducks and shorebirds depend on benthic organisms
(including mollusks and crustaceans), and small fish. The
density and health of duck populations are therefore control-
led by the health and numbers of these lower food chain
organisms. Potential toxic and other effects of effluents
which may influence marine birds are further discussed in
Chapter VII.
365

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REFERENCES
CHAPTER VI
Ames, Jim. November 12, 1980. Personal communication to
Kathryn Pazera, Biologist, NEC.
Aspitarte, T.R. and B.C. Sma].e. March 1972. “Sludge Bed
Survey Near Crown Zellerbach Dock, Port Angeles Inner
Harbor.” Research Memorandum No. 109—9. Project No.
912—2. 17 PP. and app.
Bishop, R.A. and R. Devitt. 1970. “A Report on the Port
Angeles Harbor Intertidal Clam and Biological Survey.”
(Technical Report 70—4). Washington Department of Ecology,
Olympia, Washington p. 30-43.
Buingarner, Richard. June 1977. Puget Sound Shrimp and Crab
Management Study. Project No. 1-97-R covering period of
July 1, 1973 — June 30 , 1976. washington Department of
Fisheries. Olympia, Washington. 41 pp.
Bungarner, Richard. March 1979. Puget Sound Crab and Shrimp
Management Study. Project No. D-77l, Segment No. 2 cover-
ing period of July 1, 1976 — September 30, 1978. Washing-
ton Department of Fisheries. Olympia, Washington. 72 pp.
Canning, D.G. 1976, 1977, 1978, 1979. Unpublished field jour-
nals. Douglas 3. Canning, Olympia, Washington.
Chester, A.D Damkaer, D. Day, and 3. Larrence. 1978. Puget
Sound Energy - Related Research Project Plankton Studies .
Pacific Marine Environmental Laboratory. Unpublished Report.
MESA Project.
Cross, J.N., K.L. Fresh, B.S. Miller, C.A. Simenstad, S.N.
Steinfort and J.C. Fegley. December 1978. “Nearshore
Fish and Macroinvertebrate Assemblages Along the Strait
of Juan de Fuca Including Food Habits of Common Nearshore
Fish, Report of Two Years of Sampling.” NOAA Technical
Memorandum ERL MESA 32, Boulder, Colorado. 188 pp.
Cumbow, R.C. (ed.). 1978. “Washington State Shellfish.” WasI —
ington Department of Fisheries. Olympia, Washington. 55pp.
Egan, Ron. April 1978. “Salmon Spawning Ground Data Report.”
Progress Report No. 51, Washington Department of Fisheries.
Olympia, Washington. 484 pp.
Egan, Ron. June 1979. “Salmon Spawning Ground Data Report,
1978-1979.” Progress Report No. 86. Washington Department
of Fisheries. Olympia, Washington, 91 pp.
366

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Egan, Ron. May 1980. “Puget Sound Salmon Spawning Ground
Data Report, Water Resource Inventory Areas 1—19 For
Escapement Years 1978 and 1979.” Washington Department
of Fisheries. Olympia, Washington. 145 pp.
English, T.S. March 13, 1972. “Report on Benthic Survey
Conducted January 19-20, 1972.” IN: Sludge Bed Survey,
Research Memorandum No. 109—9. vironmental Services,
Intracompany Correspondence, Crown Zellerbach Corpora-
tion, Port Angeles, 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 pp.
Fletcher, V., P. Coleman and P. Hall. October 1979. 1978
Hatcheries Statistical Report of Production and Plantings.”
Progress Report No. 93. washington Department of Fisher-
ies. Olympia, Washington. 196 pp.
Foster, B., V. Fletcher and P. Coleman. October 1978. “1977
Hatcheries Statistical Report of Production and Plantings.”
Progress Report No. 75. Washington Department of Fisher-
ies. Olympia, Washington. 172 pp.
Frost, B.W. 1974. “ Calanus marshallae , a New Species of Cala—
noid Copepod Closely Allied to the Sibling Species C. f in-
marchicus and C. glacialis.” Marine Biology . 26: 7779.
Gardner, F. (ed.). June 1978. North Puget Sound Baseline
Program 1974-1977. washington State Department of Ecology
Baseline Studies Program, Olympia, Washington.
Geist, Richard. November 12, 1980. Personal communication to
Kathryn Pazera, Biologist, NEC.
Goodwin, C. Lynn. August 1973. “DistributiOn and Abundance of
Subtidal Hardshell Clams in Puget Sound, Washington.
Washington Department of Fisheries. Technical Report
No. 14. Olympia, Washington. 81 pp.
Goodwin, C. Lynn. August 1973(a). “Subtidal Geoducks of Puget
Sound, Washington.” Washington Department of Fisheries.
Technical Report No. 13. Olympia, Washington. 64 pp.
Goodwin, C. Lynn. January 1978. “Puget Sound Subtidal Geoduck
Survey Data.” Progress Report No. 36. Washington Depart-
ment of Fisheries. Olympia, Washington. 107 pp.
Goodwin, C. Lynn and W. Shaul. February 1978. “Puget Sound
Subtidal Hardshell Clam Survey Data.” Washington Depart-
ment of Fisheries. Progress Report No. 44. Olympia,
Washington. 92 pp.
367

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Goodwin, C. Lynn and W. Shau].. May 1978(a). “Puget Sound
Hardshel]. Clam Survey Data: March 1977 to March 1978.”
Washington Department of Fisheries. Progress Report
No. 64. Olympia, Washington. 12 pp.
Goodwin, C. Lynn and W. Shaul. May 1978(b). “Puget Sound
Subtidal Geoduck Survey Data: March 1977 to March 1978.”
Washington Department of Fisheries. Progress Report
No. 65. Olympia, Washington. 30 pp.
Goodwin, C.L. and R.E. Westley. 1970. “Port Angeles Subtidal
Clam Survey.” Washington Department of Fisheries, Olym-
pia, Washington.
Homes, L.J., W.D. Ward and G.D. Nye. 1978. “Washington
State Sport Catch Report 1977.” Washington Department
of Fisheries. Olympia, Washington. 63 pp.
Kittle, L. 1976. “Intertidal Clam Survey of Port Angeles
Harbor.” IN: Port Angeles Harbor Biological Studies,
Spring 197ST Technical Report No. 76—4. Washington
Department of Fisheries. Olympia, Washington. p.30-43.
Manuwal, D.A., T.R. Wahi and S.M. Speich. September 1979.
“The Seasonal Distribution and Abundance of Marine Bird
Populations in the Strait of Juan de Fuca and Northern
Puget Sound in 1978.” NOAA Technical Memorandum ERL-
MESA—44. Boulder, Colorada. 391 pp.
Mathematical Sciences Northwest, Inc. November 1977. “Wash-
ington Coastal Areas of Major Biological Significance,
Appendix G.” Baseline Study Program No. 11. Washington
State Department of Ecology. 651 pp.
Moore, Allen W. January 1976. “Port Angeles Harbor Field
Toxicity Tests.” IN: Port Angeles Harbor Biological
Studies, Spring 1973 . Washington State Department of
Ecology. pp.4— 9.
Northern Tier Pipeline Company. June 1979. Application for
Site Certification Submitted to State of Washington,
Energy Facilities Site Evaluation Council, Olympia,
Washington. V91ux es III and V.
Nyb].ade, Carl F. March 1978. “The Intertidal and Shallow
Subtidal Benthos of the Strait of Juan de Fuca, Spring
1976 - Winter 1977.” NOAA Technical Memorandum EEL—
NESA 26. Boulder, Colorado. 156 pp.
368

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Nyblade, Carl F. March 1979. “The Strait of Juan de Fuca
Intertidal and Subtida]. Benthos.” Second Annual Report,
Spring 1977 - Winter 1978. Prepared for MESA Puget Sound
Project, Seattle, Washington in partial fulfillment of
EPA Interagency Agreement No. D6-E693—EN. Program Element
No. EHE 625—A. United States Environmental Protection
Agency 600/7—79—213. 129 pp.
Nye, G.D. and W.D. Ward. 1974. “Washington Salmon Sport
Catch Report...From Punch Card Returns in 1973.” Wash-
ington Department of Fisheries. Olympia, Wash.in9ton. 50 pp.
Nye, G.D., W.D. Ward, L.J. Homes. 1975. “Washington State
Salmon Sport Catch Report 1974.” Washington Department
of Fisheries. Olympia, Washington. 49 pp.
Nye, G.D., W.D. Ward and L.J. Homes. 1976. “Washington State
Sport Catch Report 1975.” Washington Department of
Fisheries. Olympia, Washington. 58 pp.
Nye, G.D., W.D. Ward, and L.J. Homes. 1977. “Washington
State Sport Catch Report.” Washington Department of
Fisheries. Olympia, Washington, 60 p .
Parson, T.R. and R.J. LeBrasseur. 1970. The Availability of
Food to Different Trophic Levels in the Marine Food Chain .
University of California Press. Berkeley, California.
Phifer, L.D. 1933. “Seasonal Distribution and Occurrence of
Planktonic Diatoms at Friday Harbor, Washington.” Publi-
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Washington Press, Seattl , Washington.
Phifer, L.D. 1934. “Vertical Distribution of Diatoms in the
Strait of Juan de Fuca.” Publications in Oceanography
1(3): 83—96. University of Washington Press, Seattle,
Washington.
Puget Sound Task Force of the Pacific Northwest River Basins
Commission. March 1970. Comprehensive Study of Water
and Related Land Resources, Puget Sound and Adjacent
Waters , State of Washington. Appendix VI: Fish and
Wildlife.
Rasch, T. and R. Foster. May 1978. Hatchery Production
Investigation Catalog 1974 Brood. Hatchery Statistical
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Olympia, Washington. 68 pp.
Rigg, G.D. and R.C. Miller. 1949. “International Plant and
Animal Zonation in the Vicinity of Neah Bay, Washington.”
Proceedings of the California Academy of Science, 4th
Series . 26Tl0) : 323—351.
369

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Salo, L.J. 1975. A Baseline Survey of Significant Marine Birds
in Washington StaE . Coastal Zone Environmental Studies
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Scott, W.B. and E,J. Crossman. 1973. “Freshwater Fishes of
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Sekulich, Paul. November 5, 1980. Personal communication to
Kathryn Pazera, Biologist, NEC.
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Steinfort, and J.C. Fegley. December 1977. “Nearshore
Fish and Macroinvertebrate Assemblages Along the Strait
of Juan de Fuca Including Food Habits of Nearshore Fish.”
NOAA Technical Memorandum ERL MESA-20. Boulder, Colorado.
144 pp.
Simenstad, C.A., B.S. Miller, C.F. Nyblade, K. Thornburgh and
L.J. Bledsoe. 1980. “Food Web Relationships of Northern
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Washington State Department of Ecology. April 1978. Coastal
Zone Atlas of Washington, Volume 12: Clallam County .
DOE , OI mpiγ, Washington.
Washington Department of Fisheries. June 1976. “Washington
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Bottomfish Commercial Catch Data Based on Interviews and
Projected Totals. WDF, University of Washington Office,
Seattle, Washington.
370

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Washington Department of Game. 1975 - 1979. Summer-run
and Winter-run Stee].head as Reported for Boldt Case
Area. Treaty Indian Fisheries. WDG, Olympia, Wash-
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Washington Department of Game. 1963 - 1979. Summary of
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22 p.
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Ziligis, Gordon. December 17, 1980. Personal communication
to Kathryn Pazera, Biologist, NEC.
371

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VII. ECOLOGICAL EFFECTS
Port Angeles Harbor (hereafter Harbor) forms a partially protected
saltwater exnbayment adjacent to a high energy environment (Strait
of Juan de Fuca, hereafter Strait) which is influenced by both
oceanic and estuarine biological communities. The Strait is an
ecological transition zone between purely marine species (to
the west) and other species with marine—type salt tolerance, but
which thrive better in the shallower, lower salinity estuarine
waters of Puget Sound. In such a transition zone, ecological
communities are typically diverse, containing organisms from
both adjacent regions, but often in lowered numbers due to physi-
cal or chemical stresses in the transition area and competition
from other organisms. As a protected area, the Harbor can be
expected to naturally support both higher numbers and a higher
diversity of marine organisms than the open Strait. However,
there is evidence that current and historical effects of pulpmill
effluents combined with residual effects of pulp sludges may have
reduced natural levels.
It has been demonstrated in previous chapters of this report
that:
• pulpmil2. effluent contains compounds deleterious to
water quality and biological organisms
• significant aquatic biological resources exist in the
Port Angeles area, although populations and distri-
bution of these organisms are poorly known
• the pathways and effects of individual chemical com-
pounds on each species of organism are known only
through a few scattered experiments
The explicit modes of interaction of chemical wastes with ecol-
ogical communities near Port Angeles are totally unknown in
any holistic sense. Inferences can be drawn from known ecolog-
ical mechanisms, information on pollutants and toxic compounds
and from the limited data on biological effects using sulfite
372

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effluents at other sites. However, no definitive statements or
conclusive proofs of ecosystem degradation or non—degradation
can be shown, given the present lack of data. The remainder of
this chapter is an elucidation of the known structure and dynam-
ics of the aquatic ecosystem at and near Port Angeles and
enumeration of potential modes of influence of pulpmill wastes
on those resources.
The first section below deals with primary productivity of the
ecological system. This is basically a measure of the existence
and efficiency of photosynthetic plant organisms to convert
solar energy into chemical energy which supports all life in
the marine ecosystem. This is followed by a discussion of secon-
dary or consumer organisms which feed on plants, or each other,
forming a (food) web of species inter-relationships. This
section is followed by a synopsis of known species’ life cycles,
migration patterns, and consequent damage mechanisms from
water pollutants. The last section points out mechanisms and
potential parameters which could be used to measure changes in
the aquatic ecosystem.
A. PRIMARY PRODUCTION
Primary production estimates are generally based either on
chlorophyll concentrations or on biomass coupled with known
photosynthetic efficiency. None of these factors are well known
for Port Angeles, although some estimate of phytoplankton biomass
can be derived from known populations of diatoms and dinoflagel-
lates. Chlorophyll sampling has not been carried Out Ofl any
organized synthetic basis, although a limited amount of sampling
was carried out by the U.S. Environmental Protection Agency (EPA)
in June 1979 at seven stations (see Table VII -1).
Based on numbers of organisms, and assuming diatoms to compose
the bulk of the phytoplankton (Chester et al. 1978, Rhyther and
373

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Table Vu-i. CHLOROPHYLL DATA FROM SEVEN STATIONS: PORT ANGELES
HARBOR AND POINTS EAST, June 6 - 0, 1979
Source: Shea, 1980
Date/Depth
(in)
June 6
June 7
0i’
June 8
Station Om
5m
lOin
0
in Sm
lOin
Sm
lOin
1
—
—
—
1.0
4.3
4.5
9.5
7.2
2.1
3
—
—
—
1.5
4,2
1.0
—
—
—
4
—
—
—
1.0
6.2
1.0
—
—
—
5
—
—
—
5.4
14.0
13.0
—
—
—
6
-
—
—
6.4
6.5
5.2
-
—
-
7
—
—
—
—
7.5
3.3
—
—
—
8
-
—
—
9.5
—
-
-
-
-
9
—
—
—
—
—
—
8.4
12.0
6.0
10
—
—
—
—
—
—
9.4
12.0
1.3
1].
—
—
4.2
—
—
—
13.0
15.0
3.2
12
—
—
1.0
—
—
—
—
—
—
13
—
—
—
—
—
—
8.4
8.4
8.4
Control*
—
4.7—5.7
—
—
10.1—10.5
—
—
10,9
N_4**
—
—
6.4
2.1
1.O***
74
95
54
*
Control is Clam Bay seawater taken at 12 meters depth.
**
N—4 is a control point normally not in the effluent plume located
roughly 1 mile of f the mouth of Morse Creek
* **
taken at 30 in depth
374

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Yentsch 1957), the primary production in the Strait is apparently
considerably below that of other coastal marine systems (in the
north Atlantic coastal region) (Riley 1947, Patten 1962). Num-
bers of diatoms and dinof].agellates are generally less by a
factor of ten or more, both during normal and peak (bloom) growth
periods. This large discrepancy may be due to the more northerly
latitude and possibly lower level of sunlight intensity in the
Strait.
The Nort e-rn Tier studies (NTPC 1979) found over 60 species of
phytoplankton with rather high diversities at two stations
south and east of the tip of Ediz Hook (Table VII—2). During
winter months, these plankton apparently concentrate in deeper
waters, rising to the surface during spring and summer when
photosynthetic activity is higher. These organisms would tend
to encounter and be affected by effluents most in surface waters
where their photosynthetic efficiency is normally highest.
Chlorophyll levels in June 1979 tended to be highest at the
5 meter level, indicating that the major portion of the planktonic
productivity probably occurs between 2 and 5 meters of depth.
There is a distinct depression of chlorophyll levels at both
surface and 5 meter depths (Figure Vu—i) in the effluent plume
near the diffuser. Data from stations more than 1500 meters east
of the diffuser were consistently far below 6 mg/rn 3 . At 5 meter
depth, the closest 2 stations showed 4.2 and 4.3 mg/rn 3 while
surface stations showed values below 15. This represents a
decrease in primary productivity to between 20 and 50 percent
of normal levels close to the diffuser, and generally depressed
levels for at least 3000 meters. However, stations west of the
diffuser (Station 10) which were not in the effluent path
showed normal chlorophyll levels. The fact that phytoplankton
move with the currents indicate that the inhibitory effects
on photosynthesis must be sudden and drastic in order to pro-
duce the effects measured. This loss of primary production
due to pulpmill effluents can be expected to decrease the
375

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Table VII-2. ORGANISM ABUNDANCE AND DIVERSITY AT TWO PORT ANGELES HARBOR STATIONS,
FEBRUARY AND APRIL 1978
Source: NTPC 1979
DENSITY (units
per liter)
Station 3
Station 5
L, 3, 5 m 7, 9, 11 m
1, 3, 5 m
7, 9, 11 m
Month
Parameter
Composite Composite
Composite
Composite
Mean SD Mean SD
Mean SD
Mean SD
February
Total Individuals
3,276 1,551 9,834 2,370
18,266 1,140
16,277 4,010
Total Taxa
25 36
54
37
Diversity
3.00 3.21
3.76
3.42
Maximum Diversity
4.58 5.13
5.58
5.13
Equitability
65.38 62.67
67.43
6.66
April
Total Individuals
99,479 5,720 63,453 2,980
59,585 31,610
43,171 2,790
Total Taxa
48 43
44
42
Diversity
3.47 3.10
3.40
3.35
Maximum Diversity
5.28 5.17
5.21
4.95
Equitability
73.27 59.97
65.24
67.71

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44
14
Figure Vu-i. Chorophyll a at 5 Meters Depth as a Function of
Distance East of the ITT Rayonier Diffuser; June 7, 1979.
r 1
nil
I-I
‘ —I
Di
0
I .’
0
I -I
C)
.
.
Distance from Outfall Cm)

-------
biological energy necessary to sustain higher levels of the
food webs.
B. SECONDARY PRODUCTION AND FOOD WEBS
Sixnenstad, et. al. (1979) has constructed seasonal aquatic food webs
for zooplankton, invertebrates, and their predators based on studies
of zooplankton at Morse Creek, Dungeness Spit, and other locations
on the Strait (Appendix VII—A). Simenstad has constructed more general
food webs from these seasonal studies which are roughly representa-
tive of specific substrate and habitats.
Figure VII-2 shows a protected sand—gravel sublittoral (benthic)
food web which represents the sum of seasonal webs inside Ediz Hook
and at Morse Creek, east of Port Angeles Harbor, both of which
have eelgrass beds with sand-gravel substrate. Based on studies
of mill effluents (sulfite where known) the figure indicates
potential direct and indirect (through feeding) toxic effects on
these organisms. Figure VII-3 and VII—4 show food webs along a
rocky shoreline, probably representative of high energy areas
outside Ediz Hook (data is from the North Beach area). Simenstad
has also constructed a generalized food web for the nearshore
waters Cneritic zone) away from the beach zones as shown in
Figure VII—5. Potential toxic effects of mill effluents are also
indicated for this food web, which may approximate conditions
found in Port Angeles Harbor, although differences are likely due
to the sheltering effect of Ediz Hook and the impacts of histor-
ical and present pollutant discharges. It should be noted that
the seasonal food webs in Appendix Vu-A are not comprehensive
and do not include certain key species (i.e., clams) and that
the more general webs shown in this chapter are, to some extent,
extrapolations; however, these diagrams do help to give concep-
tual structure to important benthic and neritic communities.
378

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BUFFALO
SCULPIN
PACIFIC —
$T GHORN
: SCULPIN
_-
PRIMARY 75—100% of total I A I I I —
SECONDARY 50— 74% of total I.RJI
TERTIARY 125 -49% of total l.R.l.p
— — — INCIDENTAL 110 — 24% of total l.R.l. I
Figure VII-2. PROTECTED SAND-GRAVEL/EELGRASS SHALLOW SUBLITTORAL FOOD WEB, PORT ANGELES AREA
(BECKETT POINT DATA - APPLICABLE TO INNER EDIZ HOOK AND MORSE CREEK SHORELINES)
GREATER --
TELLOWLEGS.
5ANPERUNG.
—— LEAST.& _____________
——- -—--—
WISIERN SNOW GOOSE.
CANADA GOOSE,
SNAKE
$*NDPI PER
AMERICAN COOT
BLACK BRANT
____J - I ouTJ ___
.4 ’
44 Li UNNEL GUNNEL ,, I.
I I I
I ‘‘ I VINILEI 1 Jf iE iIi tj,f____.__. 1 s C—O SOLE
i ______
NlJ
UNCPACIPIC., I
// I UBENOSE
ANPLANC ,
4- - L -

_______ )r
\; t1, ak” P ACHE
f1 - ‘ --- L {NEMERTEAN t’
/ TANAIDS I ’ — I
ARPACTICOID I
‘/iIG*s1RoPnJ J I CUMACEAN4 H COPEPODS P 1POD$ ANNELIDS MYSIDS
POLYCI4AETE 1
— --I-
Iv*wwui*s GURID o p I — “1
ACHYURAN θ I IPERAN
I CRABS CRABS I$OPODS
—
- BENTHIC - / /
‘ IMICROPHYTIC j
ALGAE
NACII O.HThQ’
I
EELGRASS
_____ DIrectly .lf.ctsd [ I Directly affected
________ Isulistil -- - — 10th.’ pulp sffluentll
[ j — Indi.ctly affected u h%dlf.CIIV affected
________ laulfitel I — lother pulp e lf iu.nisi
Source: Simenstad 1979

-------
— PRIMARY 11 5- 100% 01 lolsI IKLI
— UCONGAIIY ISO—M%oI 1.1.1 LRLI
—— TERTIARY I35—4 5%.l 1.1.1 I*LI
INCRIENTAL 110— 24% .1 otsI IRS
N0NTh
______ I SEA LI0 ’ NO NOES
MAR ION
CC AN1 — r”- — — __
‘I —
LAD ‘
CABEZON
_________ IN J
—— _ ;• — — — —— ‘Z LA:INS] — SEAL
iLASTAAR / PUGE — — — — — —
LIP ‘
_______ ______ ______ _______ ______ LONGFIN
4 II, Ij(re!ir 1fF&* _____
_____ _____ _____ _____ COPPER :
I,
/1 _______
i __________ FISHES INC ACICETE STRIPED
,#,/ , // t i / SCHOOLING ‘t V / SCU N I _________
LARVAL LANCE HERRING. 1 4i’ t i COST [ APERCH I
P— r CIFIC SANG
._, : JUVENILE
, GADIDS AND
, ;, , // I I /
/ / I
t ..
I, /
I
III %NMTOOIIATRS OPAl
I, /
I
I, I I
,, % %%% HYPERIID LARVAL
IPREDATORY // I S
____ __
.‘, 1 ______
/ j G TR O J PORIFERANS.\ 4 CALANOID
ASCIDIACLANS • COPE PODS GAMMASID
,, f v ° ’ /
‘I ___________
NOACHIOPODS • AMPHIPOOS
i / CNI RIAIIS I SRACHYURAN ___________ I,
IRYOZOAN$ I _____________ _______________
ISOPOOS
CRASS I POLYCHAITE
CRUSTACEAN J ANNELIDS i 1 FLASELUFLRAN
________________
NAUPLII
1 ASALONE SCALLOPS
GRAZING SEA /
__________ ___________________
___ :1 FSEN ______
GAITIOPODS _________________
- - 15
_____________ LANK TON I MEIOFAUNA
____ _ __ ___ gl
.I [ PAGURIO7 fI ,
____________ CRASS J
I _d’ I MACROPHYT
/ I ALGAL
— MICRGPNYT
‘Si
Figure VI—3.
COMPOSITE FOOD WEB CHARACTERISTIC OF SUBLITTORAL (SUBTIDAL-BENTHIC) ROCKY!
KELP BED HABITATS IN NORTHERN PUGET SOUND AND THE STRAIT OF JUAN DE FUCA
Source: Simenstad 1979

-------
PRIMARY 175100% of total l.RJ.I
SECONDARY 150—74%oI total l.R.LI
— TERTIARY 125—49% of total LRJ.l
— — INCIDENTA 110— 24% of total LRI. I
Figure VII-4. COMPOSITE FOOD WEB CHARACTERISTIC OF ROCKY LITTORAL HABITATS IN
NORTHERN PUGET SOUND AND THE STRAIT OF JUAN DE FUCA
Source: Simenstad 1979

-------
NON —FEEDING
ADULT PINK.
CHUMS COHO,
CHINOOK, AND
SOCKEYE SALMON.
STEELHEAD TROUT,
AND
PACIFIC HERRING
PRIMARY 75—100% of total (RU
SECONDARY 50—74% of total (RH
TERTIARY 125 —49% of total IRJ.I
INCIDENTAL 110— 24% of total LRJ.I
Figure VII-5. NERITIC FOOD WEB, PORT ANGELES AREA
Source: Simenstad 1979
I GA/
— DIRECTLY AFFECTED
lull It• I
— INDIRECTLY AFFECTED
IsuIlIt• I

-------
Several factors are of immediate importance pertaining to potential
long-term ecological effects or to concentrations of toxic com-
pounds in the food chain. First, much of the important secondary
biological production utilizes detritus (organic particles) which
remain in the water column or in the bottom sediments for some
time, allowing the chance for these particles to become bound to
pollutant compounds (through coating action, molecular attraction,
absorption, etc.). Secondly, phytop].ankton produce most of the
systems’ energy fixation. These organisms are affected by any
pollutant which reduces water clarity. Pulpmill effluents are
known to reduce light transmittance and have also been shown to
be toxic to phytoplankton (Eloranta and Eloranta 1974, Moore and
Love 1977). Third, the food web contains several stages or
levels before a food source reaches fish, birds, or other pre-
dators, allowing for several stages of bioaccumulation of
compounds.
As toxic compounds are taken up by organisms and later transmitted
to other elements of the food chain, toxic effects may increase
due to:
• cumulative buildup in an organism
• synergistic effects in combination with other toxic
compounds
• accumulation and concentration in biological food
chains
While insecticides, herbicides and other chemicals have been
studied in some detail (Macek 1970, Macek and Korn 1970, Odum
1971), there is little literature on such effects from pulpmi].l
wastes. Toxicity studies have tended to focus on short-term
acute affects, and even here, kraft effluents have been subjected
to more research than sulfite effluents. The lack of literature
indicates only lack of study rather than lack of effects. Many
of the compounds found in pulpinill effluent are in chemical
families of known ecological toxicity such as heavy metals,
chlorinated hydrocarbons, terpenes, phenols, and resin acids
383

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(Becker and Thatcher 1973, Easty et al. 1978, Hutchins 1979).
Toxic effects of these effluents have been demonstrated for
sulfite effluents for both salmonid and (to a lesser extent)
non-salmonid marine organisms as demonstrated in Figures VII-2
and VII—5.
C. DAMAGE MECHANISMS
Most ecological damage basically occurs 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 addition, effluent
effects on habitat (such as sediments) may change these same fac-
tors. In this section, damage mechanisms are discussed in terms
of organismic effects. Ecosystem implications are discussed
in Section VII. D. 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-
ogica1) 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.
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Not all organism deaths can be expected to be evident during a
96—hour bioassay. Early studies with sulfite mill effluent
(WDF 1960) showed that the majority of fish ( Oncorhynchus kis-
utch ) tested often survived a 96-hour exposure to 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 method
of determining such long—term effects would be chronic
bioas says.
Physiological or morphological abnormalities induced by exposure
to detrimental compounds can potentially decrease an organism’s
survival in its natural habitat. Most of the studies of such
sublethal abnormalities have been conducted with sulfite or kraft
mill effluent and are summarized by Hutchins (1979), although
lethal effects of sulfite effluent (without secondary treatment)
have been found for salmon and trout (Kondo et al. 1973, Rosehart
et al. 1974, Wilson 1972, Wilson and Chappell 1973). In addition,
physiological changes 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 l971a, l971b)
• reduced swimming speed (Seppovara 1973)
Other metabolic and morphological disturbances which have been
noted for other types of effluent, but which are not covered in
the sparse literature on sulfite effluent include:
• inability to feed properly (through morphological
or behavioral change)
• altered predator/prey relationship (changes in camou-
flage,ability, growth rate, etc.)
• malfunction of body parts (through morphological or
physiological cause)
385

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• altered relationship with own species due to abnor-
mality (this could be potentially important in
species which congregate for protection)
• increased susceptability to disease
• osmoregulatory imbalance
Reduced feeding in salmon, crustacean and invertebrates as a
response to sulfite and kraft effluents has been documented by
Davis (1973), Ellis (1967), Tokar and Owens (1968), Gazdziaus—
kaite (1971ΰ, 1971b), and McLeese (1970). There are no well
known feeding studies on mechanical mill effluent. Changes in
swimming speed or growth rate have been demonstrated by Tokar
and Owens (1968), Webb and Brett (1972), and Howard (1975).
Numerous body function changes have been demonstrated under
laboratory conditions including circulatory changes, respira-
tion problems, metabolic and historical changes (Walden et al.
1970, McLeay 1973, Holland et al. 1960, etc.). More subtle fac-
tors such as altered inter- or intra-species interactions,
increased susceptability to disease or osmoregulatory imbalance
have not been well studied for mill effluents, but are well-
known effects from other toxicants (Ferguson 1970, Livingston
et al. 1975, Leadem et. al. 1974, and Brown 1978).
Other effects could be hypothesized; however, the above list
shows several ways in which morphological or physiological
changes can reduce an organism’s competitive survival probability
in its normal habitat.
Behavioral changes may also inhibit the ability of aquatic
organisms to compete in their habitat or complete necessary parts
of their life cycle. This is particularly important in the case
of anadromous fish, whose spawning and migration instincts de-
pend on a highly developed sensory pattern. Upset of subtle
physiological factors can cause non—migratory or incorrect
spawning behavior, resulting in lowered spawning success for the
species as a whole. Behavioral studies of fish in response to
pulpmill effluent have been largely limited to avoidance behavior
386

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in the laboratory (Hutchins 1979) and no data on spawning effects
are known.
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.
A toxicant may affect aquatic organisms by exerting non-visible
physiological stress, either physical or chemical. Such stress
usually interacts in a cumulative or synergistic manner with
other stresses exerted on the organism by its environment and may
influence survival ability (Ferguson 1970, Hutchins 1979). The
visible manifestations of such combinations have been discussed
in terms of susceptibility to disease, osmoregulatory upset, etc.;
however, less obvious effects are likely to result merely in
“death from unknown causes” in laboratory experiments or the
natural environment. Such effects have not been studied and
would be very difficult to document, except at a biochemical
level.
The effects of these various damage mechanisms manifest themselves
to organisms higher in the food chain both by consumption of
toxic substances in prey organisms, or by a reduced availability
of food. Toxicity may become increasingly concentrated as the
top of the food chain is reached. Studies of heavy metal toxi-
cants and PCB’s have shown that these substances may become
concentrated by factors of several hundred to several thousand
at each step in the food chain (Harris 1971, Macek and Korn 1970,
Lowman et a].. 1971). Many of the chemical elements and compound
families associated with pulpmill effluents do have this potential.
Thus both bio—accumulation of toxicants and reduced viability
387

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of food organisms can be expected to most severely affect organ-
isms at the top of the food chain, notably man.
D. ECOSYSTEM EFFECTS
There is at present little data on Port Angeles area ecosystems
with which to assess either “natural” functioning of the eco-
system or the effects of pulpmill effluents or other pollutants.
The main parameters of importance in assessing such effects are:
• primary productivity
• secondary productivity
• ecosystem diversity
• ecosystem stability
• synergistic effects
• import, storage, and
export of pollutants
A few studies have been conducted (Eloranta and Eloranta 1974,
Rainville et al. 1975, Stockner et al. 1975) which show that
phytoplankton productivity can be adversely affected by pulp—
mill effluent toxicity. Chlorophyll tests conducted at Port
Angeles in 1979 show a rather substantial reduction in chloro-
phyll, and hence primary production near the ITT Rayonier diffuser.
Additionally, effluent opacity to light can be expected to re-
duce photic zone productivity to a minor extent. Zimmerman
and Livingston (1976) have found mill effluent to similarly
affect macroscopic and benthic algae.
Loss of secondary productivity for aquatic ecosystems has been
documented only from toxicity tests, conducted on the organismic
and species levels. The only other data which approximates
productivity data are various fish seine samples taken east of
Port Angeles Harbor (Cross et al. 1978). Even these data are
not long—term and consistent enough to evaluate any potential
effects from effluents. However, the numerous studies which
388

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exist on effluent effects on aquatic organisms do indicate a
definite potential for deleterious effects on secondary produc-
tivity in general (Cooley 1977, Livingston et al. 1975, Harger
et al. 1973)
The only direct indication of ecosystem diversity has been carried
out for species richness in fish by Cross et al. (1978) (see
Table VI-K-l, Appendix VI-K). Species richness as measured in beach
seine samples was shown to be somewhat lower at Dungeness Spit
than at Morse Creek. This could be due to habitat differences
or a result of the higher energy environment at Dungeniess Spit.
Some diversity is contained in Northern Tier studies of the
Harbor, due to methodological differences, these data are not
comparable with Cross et al. (1978).
With little knowledge of basic ecological parameters such as
productivity, diversity and ecosystem functions, one cannot
extrapolate stress on those ecosystems. The ecological literature
generally presumes, however, that physical stresses induced by
pollutants and toxicants break or weaken key links in the eco-
system, thus contributing to an overall decrease in long—term
stability. Such stability decrease can be amplified through
synergistic interdependencies among biological organisms.
The last and perhaps the most important unanswered question is
that of pollutant fate in the aquatic ecosystems in Port Angeles.
Although currents and oceanographic dynamics in the area can be
quantified to some extent (see Chapter VIII), measurements of
pollutant export from the area and pollutant storage within the
area due to storage in sediments is virtually unknown. In the
1950’s and 1960’s, pu].pmill effluents resulted in significant
buildups of sludge and volatile compounds in sediments. No
recent studies have been conducted around the relocated outfalls
to determine if this type of effect still occurs.
389

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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 pulpmi].l effluents, the
ecological 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.
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REFERENCES
CHAPTER VII
Becker, C.D. and PD. Thatcher. 1973. Toxicity of Power Plant
Chemicals to Aquatic Life. U.S. Atomic Energy Commission.
Washington, D.C.
Brown, A.W.A. 1978. “Effects of Organochiorine Insecticides
on Fish.” IN: Ecology of Pesticides . Wiley-Interscience
Publication. J En Wiley & Sons, New York. 180 pp.
Chester, A.D. Damkaer, D. Day and 3. Larrence. 1978. Puget
Sound Energy - Related Research Project Plankton Studies.
Pacific Marine Environmental Laboratory. Unpublished
Report. MESA Puget Sound Project.
Cooley, J.M. 1977. “Filtering Rate Performance of Daphnia
retrocurva in Pulpmill Effluent.” Journal of Fisheries
Reasearch Board of Canada . 34:863—868.
Cross, Jeffery, K.L. Fresh, B.S. Miller, C.A. Simenstad, S.N.
Steinfort, J.C. Fedgley. December 1978. “Nearshore Fish
and Macroinvertebrate Assemblages Along the Strait of Juan
de Fuca, Including Food Habits of the Common Nearshore Fish,
Report of Two Years of Sampling.” NOAA Technical Memorandum
ERL MESA—32. 188p.
Davis, J.C. 1973. “Sublethal Effects of Bleached Kraft Pulp
Mill Effluent on Respiration and Circulation in Sockeye
Salmon ( Oncorynchus nerka). Journal of Fisheries Research
Board of Canada . 30:369.
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 Re-
ceiving Waters.” Vatten 1:36—48.
Ellis, R.H. 1967. “Effects of Kraft Pulp Mill Effluent on
the Production and Food Relationships of Juvenile Chinook
Salmon in Laboratory Streams.” Technical Bulletin No. 210,
NCASI. New York, N. Y.
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.
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Gazdziauskaite, I.B. 1971 a. ‘ t Effects of Effluents from the
Sovetsk and Neman Mills on the Biology of Pontoganunarus
robustoides. ” (1) Vitality. (2) Respiration intensity.
Liet. •TSR Mokslu. Adad. Darbai Ser. C. No. 2:93. CAb.
Bull. Paper Chem. 43:10694).
Gazdziauskaite, I.B. 1971 b. ‘ Effects of Effluents from the
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. Paper Chem. 43:3026).
Harger, J.R.E., M.L. Campbell, R. Ellison, W.P. Lock, and W.
Zwarych. 1973. “An Experimental Investigation in Effects
of Pulpmill Effluent on Structure of Biological Communities
in Alberni Inlet, British Columbia.” Part I and Part II.
International Journal of Environmental Studies (4) :296—282
arid (5):l3—19
Harris, Robert C. July 1971. “Ecological Implications of
Mercury Pollution in Aquatic Systems.” Biological
Conservation . Vol 3, No. 4. p.279—283.
Holland, G.A., Lasater, J.E., Neumann, E.D. and Eldridge, W.E.
1960. “Toxic Effects of Organic and Inorganic Pollutants
on Young Salmon and Trout.” Res. Bull. No. 5. State of
Washington Dept. of Fisheries. Olympia, Washington.
Howard, T.E. 1975. “Stamina of Juvenile Coho Salmon in Pulp
Mill Effluent and in Water After Effluent Exposure.”
Journal of isheries Research Soard of Canada . 32:789.
Hutchins, F.E. 1979. “Toxicity of Pulp and Paper Mill Effluent:
A Literature Review.” Corvallis Environmental Research
Laboratory. EPA-600/3-79-013.
Kondo, R., K. Sameshim 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.
Leadem, T.P., R.D. Campbell and D.W. Johnson. 1974. “Osmoregu-
larity Responses to DDT and Varying Salinities in Salmo
gairdneri - I. Gill Na-K-Atpase.” Comp. Biochem. Physiol .
49A (197—205)
Livingston, R.J., C.R. Cirpe, R.A. Laughlin and F.G. Lewis III.
1975. “Avoidance Responses of Estuarine Organisms to Storm
Water Runoff and Pulp Mill Effluents.” IN: Estuarine
Processes Vol I: Uses, Stresses and Adaptation to the
Estuary . October 7-9, 1975. Third International Estuarine
Research Conference. Galveston, Texas. 541pp.
392

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Lowman, F.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 of Sciences. Washington, D.C. pp. 161-199.
McLeay, D.J. 1973. “Effects of 12-h and 25-day Exposure to
Kraft Pup Mill Effluent on the Blood and Tissues of
Juvenile Coho Salmon ( Oncorhynchus kisutch ) .“ Journal
of Fisheries Research Board of Canada . 30:395.
McLeese, D.W. 1970. “Behavior of Lobsters Exposed to Bleached
Kraft Mill Effluent.” Journal of Fisheries Research Board
of Canada . 27:731.
Macek, K.J. 1970. “Biological Magnification of Pesticide
Residues in Food Chains.” IN: Biological Impact of Pesticides
in the Environment . (J.W. Gellet, ed.) Oregon State
University, Environmental Health Sciences. Corvallis,
Oregon. 7 70pp.
Macek, K.J. and S. Korn. 1970. “Significance of the Food
Chain in DDT in Fish.” Journal of Fisheries Research Board
of Canada . 27(8) :1496—1498.
Moore, J.E. and R.J. Love. 1977. “Effect of a Pulp and Paper
Mill Effluent on the Productivity of Periphyton and Phyto-
plankton.” Journal of Fisheries Research Board of Canada .
34:856—862.
Northern Tier Pipeline, Company. 1979. Application for Site
Certification. Submitted to State of Washington, Energy
Facilities Site Evaluation Council. Olympia, Washington.
Volume III and V.
Odum, Eugene P. 1971. Fundamentals of Ecology . Third Edition.
W.B. Saunders Company, Philadelphia. 574pp.
Patten, B.C. 1962. “Species Diversity in Net Phytop].ankton of
Raritan Bay.” Journal of Marine Research . 6:54-73.
Rainville, R.P, B.J. Copeland and W.T. McKean. 1975. “Toxicity
of Kraft Mill Wastes to an Estuarin Phytoplankton.”
Journal of Water Pollution Control Federation . 47:487—503.
Rhyther, J.H. and C.S. Yentscli. 1957. “The Estimation of
Phytoplankton Production in the Ocean from Chlorophyll
and Light Data.” Limnology and Oceanography 1:281-286.
Riley, G.A. 1947. “Factors Controlling Phytop].ankton
Populations on Georges Bank.” Journal of Marine Research
6:54—73.
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Rosehart, R.G., G.W. Ozburn and R. Mettinen. June 1974.
“Origins of Toxicity in Sulphite Pulping.” Pulp and
Paper Magazine of Canada 7c(6): 63—66.
Seppovaara, 0 . 1973. “The Toxicity of the Sulfate Pulp Bleaching
Effluents.” Paperi ja PUU . :713. CAb. Bull. Inst.
Paper Chem. 44:10910).
Seppovaara, O.and P. Hynninen. 1970. “On the Toxicity of
Sulfate Mill Condensates.” Paperi ja Puu . 52:11 (Ab.
Bull Inst. Paper Chein. 41:487).
Simenstad, C.A., B.S. Miller, C.F. Nyblade, K. Thornburgh,
and L.J. Bledsoe. 1979. Food Web Relationships of North
Puget Sound and the Strait of Juan de Fuca . Prepared for
MESA Puget Sound Project, NOAA.
Simenstad, C.A. Unpublished Data, 1977-1978. NOAA-MESA data
collected by Fisheries Research Institute. University of
Washington. Seattle, Washington.
Stockner, J.G., D.D. Cliff and K. Muuro. 1975. “The Effects
of Pulpmill Eflfuents on Phytoplankton Production in Coastal
Waters of British Columbia.” Fisheries Marine Services
Research and Development Technical Report 578. pp. 1-99.
Tokar, E.M. and Owens, E.L. 1968. “The Effect of Unbleached
Kraft Pulp Mill Effluents on Salmon. I: Growth, food
consumption and swimming ability of juvenile chinook salmon.”
Tech. Bull. No. 217, NCASI. New York, N.Y.
Walden, C.C., T.E. Howard and G.D. Fround. 1970. “A Quanti-
tative Assay of the Minimum Concentration of Kraft Pulp
Mill Effluents which Affect Fish Respiration.” Water
Res . 4:61.
Washington Department of Fisheries. 1960. “Toxic Effects of
Organic and Inorganic Pollutants on Young Salmon and Trout. t ’
Research Bulletin No. 5. Olympia, Washington. 252pp.
Webb, P.W. and J.R. Brett. 1972. “The Effects of Sublethal
Concentrations of Whole Mill Bleached Draft Pulp Mill
Effluent on the Growth and Food Conversion Efficiency of
Underyearling Sockeye Sa]..inon.” Journal of Fisheries
Research Board of Canada . 29:1555.
Wilson, M.S. and Chappell. 1973. Reduction of Toxicity of
Sulfite Effluents . CPAR Report No. 49-2. Canadian Forestry
Service. Ottawa, Ontario.
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Wilson, R.C.H. 1972. “Acute Toxicity of Spent Sulfite
Liquor to Atlantic Salmon ( Sa].mo salar ) .“ Journal of
Fisheries Research Board of Canada . 29:1225-1228.
Woelke, C.E. 1960. Effects of Sulfite Waste Liquor on the
Normal Development of Pacific Oyster (Crassostrea gigas)
Larvae . Res. Bull. No. 6. State of Washington Department
of Fisheries. Olympia, Washington.
Zimmerman, M.S. and R.J. Livingston. 1976. “Effects of Kraft
Mill Effluents on Benthic Macrophyte Assemblages in a
Shallow—bay System (Apalachee Bay, North Florida, USA).”
Marine Biology . 34:297—312.
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VIII. ANALYSIS AND RESULTS
This chapter presents analyses of oceanographic dynamics,
water quality and biological effects which can be constructed
from the existing literature and in addition presents data and
results from special studies undertaken by the U.S. Environmental
Protection Agency (EPA) and the project team and authors of this
report. oceanographic dynamics and effluent dispersal were
analyzed on a hydraulic tidal model of the Strait of Juan de
Fuca (hereafter Strait) constructed by Evans—Hamilton, Inc.
(EHI). Field studies of physical characteristics, water quality
and effluent toxicity were carried out in June, 1979 by the EPA
with field assistance from NEC and EHI. Additionally, aerial
photographs were taken of the entire area by EPA (including
multi-spectral scanner analysis) several weeks before sampling
and from an overhead plane during field sampling. The aim of
both the hydraulic model and the field studies was to define
the track of the effluent plume and to attempt to correlate
effluent with water quality and biological effects.
The chapter begins with analyses of water dynamics and efflu-
ent path and dispersion. These analyses are supported by both
field studies and the hydraulic model studies conducted by EHI.
Due to a relatively complete historical information base,
considerable analyses of these physical dynamics have been pos-
sible. The following sections provide results of water quality
analyses and discussions of biological (including bioassay)
effects which may be induced by pulpmill effluents. In these
sections, the historical data base has been found to be much
less complete, and much of the analysis is of a less quantita-
tive nature.
A. OCEANOGRAPHIC DYNAMICS
Water dynamics in the Harbor and adjacent Strait are analyzed
below using a combination of field data and data from the EHI
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tidal hydraulic model described in Chapter III. The model
simulates tidal, current, bathymetry and shoreline effects
but neglects wind and coriolis force due to practical con-
siderations. Model results have been recorded in time lapse
(streak) photographs. Water dynamics are discussed below in
terms of tidal eddys and mean currents, followed by subsec-
tions pertaining to pollutant residence time and dispersive
characteristics.
1. Tidal Eddies
The streak photographs taken of the hydraulic tidal model
reveal numerous eddies caused by the interaction of the tidal
flow and the irregular shoreline. Figure VIII-l shows the
photographs rendered to show flow direction (but not speed)
at selected tidal stages for a spring tide. Patterns of water
movement that appear closed are termed tidal eddies. These
eddies are transient features. During their existence there
may not be sufficient time for a hypothetical water parcel to
traverse their circumference; however, their positioning sig-
nificantly affects water parcel movement in the nearshore
portion of the Strait. On the flood tide five prominent
eddies (El - ES) develop to the east of the various points and
spits, and on the ebb tide seven eddies (E6 - E12) are evi-
dent to the west of the points and spits(Figure VIII-l).
The existence of tidal eddies along the Port Angeles shoreline
are suspected of being a cause or manifestation of the influences
which drive a net countercurrent eastward along the shoreline
between Port Angeles and Dungeness Spit. Due in part to this
countercurrent, pulpmill effluents disperse directly eastward,
contrary to the normal net flow direction of the Strait. Al-
though the eddies are somewhat transient features, whose exis-
tence is keyed to tidal stage, they entrain considerable
amounts of water (as evidenced by their large diameters - see
subsection “a” below) and can thus strongly influence net trans-
port of pulp effluent.
397

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I
DEL.INSETSHOWSTID P E
E6 E12 (BOTTOM) AS SEEN IN HYDRAUL
VIII-l. LOCATIONS OF FLOOD EDDIES El - E5 (
398

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a. Eddy Growth : Inspection of the tidal current patterns in
Figure VIIi-2 shows that many of the eddies grow in diameter
from the beginning to end of both flood and ebb tidal phases.
In order to demonstrate this growth the mean diameters of
eddies El, E2, E3, E5, and E12 were scaled from the streak
photographs at selected tidal stages. Although there is con-
siderable uncertainty of prototype diameters as computed from
the tidal model photographs, the growth of eddy diameter with
time is evident (Figure VIII-3). The diameter growth with
time is approximately linear at a rate on the order of 0.6
km h 1 . During major ebbs and floods the diameters of some
eddies increase as much as tenfold. Since the area contained
within an eddy increases approximately as the diameter squared,
some eddy areas increase a hundredfold.
Near the end of a tidal phase at high and low waters some of
the eddies apparently are displaced from their growth sites
and decrease somewhat in diameter. As they migrate away from
shore they contribute to the irregular flow patterns that are
evident near high and low tides. Thus it is near so-called
slack tides that greatest dispersion of the effluent is likely
to occur.
b. Eddy Dynamics : Some current measurements have been made
in three of the eddies (E3, E5, and E] .2) so that some estimate
of the dynamical balance of forces may be made. Here we
asswne that the eddies are in a steady state and the force
balance consists of terms associated with the horizontal
pressure gradient, Coriolis effect (fv) and the centrifugal
force (v 2 /r), where f is the coriolis parameter, v is the tan-
gential speed, and r is the eddy radius. Estimates of the Cor—
iolis and centrifugal force terms are described below for the
eddies which develop near the two spits.
Dungenesa Spit: Some observations of the currents in the eddies
(E5 and E12) that develop near Dungeness Spit are shown in Figure
399

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- -
—

— — -. — ‘ —
! 7 T _ __
igure VII 1-2. SURFACE TIDAL CURRENT PATTERNS IN
THE HYDRAULIC TIDAL MODEL
INSET SHOWS TIDAL PHASE
400

• — — -
— —c — ————- —
:- — —
- _ - -- -::----- —.
—
— —=--- —.
- - -z

=
32 \
I

-------
I THE HYDRAULIC TIDAL MODEL
1 (continued) r INSET SHOWS TIDAL PHASE
401

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I THE HYDRAULIC TIDAL MODEL
(continued) INSET SHOWS TIDAL PHASE 1
I
402

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Figure VIII-3. AT El., E2, and E3 (A) GROWTH OF TIDAL EDDIES, (B) IN
THE HYDRAULIC TIDAL MODEL • DOTS MD CIRCLES DENOTE
RESPECTIVELY DIAMETER DURING EDDY GROWTH AND DECAY.
IN (C) TIDAL PHASES ARE SHOWN BY DOTS ON TIDE CURVES.
403

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ViIi-4. The current vectors shown were obtained from current
meter records listed in Table 1 1 1-A—i using methods described
earlier. These eddies have also been observed using a high
frequency radar system. The results of the observations were
maps every 1 - 3 hours of currents near the surface (0—½m depth)
averaged within a grid size of 1.2 km during July 5 — 10, 1979
(Frisch 1980).
The flood eddy (E5) has been resolved in a hydrodymanical nu-
merical model of the Straits of Juan de Fuca and Georgia by
Crean (1978). The model simulates barotropic mixed tides and
uses a grid size of 2 km for computation. The model has been
compared favorably with observations of tides and tidal currents
at a number of locations by Crean (1978), and with drogue tra-
jectories in another tidal eddy south of Vancouver Island by
Crean (1978).
The results from the numerical and hydraulic models and current
measurements appear sufficient to provide some estimates of the
Coriolis and centrifugal forces in the eddy perimeters. For
the flood eddy (E5) the diameter as scaled from the streak
photographs is approximately 5 km; the mesh size for the radar
observations and numerical models are too coarse for this pur-
pose. Estimates of the tangential speed are: current measure-
ments (HNOS 21) v=20 cm s ; radar measurements (July 5, 1979
at 1800), v=30 cm s 1; and numerical model, v=20 cm s 1 . Sub-
stituting v = 20 cm s 1 , r = 5 km, and f = 1.1 x i.cr 4 (at
48.2°N) we obtain 2. x l0 cm s and v 2 /r = 2. x cm
Within the uncertainty of our parameters the two forces are of
the same order.
For the ebb eddy (E12) the diameter scaled from the streak
photographs is approximately 4 km and the tangential speed from
the current measurements (HNOS 20), v 80 cm s . Substituting
these values yields fv =--9. x i0 cm 2 and v 2 /4 = 30. x i0
cm Thus in the ebb eddy the centrifugal exceeds the CoT-
iolis force by threefold.
404

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a) CURRENT MEASUREMENTS
15’ 10’ 5’ 123
I 5• I I I I I I I I I I I I I I I I I I I I
‘ 60
I I I I I I I I I I I I I I 1123.
IS’ 10’
b) MODEL PHOTOGRAPH
—I
Is
a
48’
10’
SI
Figure VIII-4. FLOOD TIDAL EDDY E5 NEAR DUNGENESS SPIT.
Upper panel shows average flood direction
(solid arrows) and speed (cm s l) near surface
based upon current meter measurements at 12
sites (dots), and results from HF radar mea-
surements (solid arrows without dots) taken
by Frisch (1980). Lower panel shows streak
photograph taken of the hydraulic tidal model.
48’
10’
5’.
‘-V
1’ -,

SPEED(cm ’)
.1 - ‘
%‘
\ \ \l blt
‘I •‘1
b 20
• .
15•
I I I
IS’
46’
10’
- IS’
48’
10’
I I I I I I I I I I
IS’ 10’ 5’
1_SI
I I
123’
405

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Figure VIII-4. EBB TIDAL EDDY E12 NEAR DUNGENESS SPIT
continued
Upper panel shows averag ebb direction (solid
arrows) and speed (cm 8 i) near surface based
upon current meter measurements at 12 sites
(dots). Lower panel shows streak photograph
taken of the hydraulic tidal model.
406

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Ediz Hook: An expression of the flood eddy (E3) that develops
east of Ediz Hook was obtained in an infrared photograph taken
on April 25, 1979 (Figure vIII-5). This eddy has a diameter of
approximately 2 km as scaled from the hydraulic model and the
infrared photograph. Tangential speeds are: EPA, v 20 cm s ;
Tollefson Tl, v 50 cm 51; and Toilefson T2, v 25 cm s1. Sub-
stituting the mean speed of 30 cm s we obtain fv = 3. x 10
cm s 2 and v 2 /r 10 x i0 3 cm —2• Centrifugal exceeds the
Coriolis force by threefold.
An eddy (E8) develops north of and close to Ediz Hook on the
ebb tide as shown by the hydraulic model (E8; Figure VIII-l).
The diameter indicated by the hydraulic model is approximately
1 km and the tangential speed is approximately 50 cm s as
indicated by site Ti. Substituting these estimates we obtain
fv = 6. x cm s 2 and v 2 /r = 50. x l0 cm This eddy
is of sufficiently small diameter and large tangential speed
that the centrifugal force exceeds the Coriolis force by nearly
an order of magnitude.
In summary, observations of three eddies (E3, E8, and E12)
having a mean diameter of 2 — 3 km show that the centrifugal
exceeds the Coriolis force by threefold or more. The fourth
eddy (E5) had a two fold larger diameter of 5 km and the centri-
fugal and Coriolis force was approximately equal. This result
suggests that in the hydraulic model where the Corio].is force
was not incorporated, the eddies considered herein may be
adequately represented.
Other Eddies: Although there are insufficient observations to
estimate the Coriolis and centrifugal forces for eddies adjacent
to other points of land, we can estimate their diameters from
the hydraulic model. Figure VIII-3 shows the diameters for eddies
El - E12 as scaled at mid ebb and flood. The mean diameter for
eddies El - E12 is 3 km. Assuming that typical tangential
407

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a) CURRENT MEASUREMENT
28’ 26’ 123 24 22’
Jo’— I I I I I I I
SPEED (cms )
28’ 26’ 123 24’ 22’
b) INFRARED PHOTOGRAPH
2. 1 26 12324’ 22’
• j 6 1 123 t V
2
20’
— . 101
•. 6’
4r
Figure VIII-5. EDIZ HOOK FLOOD EDDY
OBSERVATIONS.
Top panel (a) shows average flood direction (solid
arrows) and speed (cm g ”l) near surface based on
current meter measurements at 4 sites (dots).
Middle panel (b) shows infrared photograph taken
by EPA. Bottom panel (c) shows streak photograph
taken of the hydraulic tidal model.
4r
8’
6’
‘ I
48’4
8’
R’
24
2? £PML 187$
SI
a
I
2.1 26’ 12324’ 22
c) MODEL PHOTOGRAPH
28 25’ t2V24’
4r
8’
4 ,
I’
22’ 20’
408

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speeds are on the order of 30 cm s then the centrifugal ex-
ceeds the Coriolis forces by twofold.
3. Impact of Exterior Tidal Flows in the Harbor
A useful measure of the kinetic energy of tidal flows is the
variance contained in current meter records. Figure VIII-6
shows a plan view of the variance as determined in depths of
0 — 20 m from historical records listed in Table III—A— i. The
pattern shows highest values of 0.2 - 0.4 m 2 2 toward mid-
channel, intermediate values of 0.1 — 0.2 m 2 2 near shore
between the two spits and the lowest value in the Harbor of
0.007 m 2 s 2 Near the Harbor mouth the variance increases
from 0.007 m 2 s 2 (at site C94) to 0.05 m 2 s 2 (at site T2)
within a distance of two kilometers. This change represents
nearly an order of magnitude increase and may be thought of
as a front of tidal kinetic energy.
Since the Harbor represents a minimum in tidal kinetic energy
it is a reasonable expectation that some energy may be trans-
ferred down the front toward the Harbor’s head. The impact
of the exterior tidal flows in the Harbor can be demonstrated
by comparing the measured variance (a m 2 ) with the variance
computed for the rise and fall of local Harbor tides. The com-
puted variance (a C 2 ) represents the average at a cross sec-
tion (A) during a quarter tidal day (z t), and was computed as
ac 2 = (TA 1 t 1 ) 2 , where T is the change in volume associated
with the diurnal tidal range landward of the cross channel
section.
Figure VIII-7 shows am 2 versus ac 2 for the Harbor and several
locations in Puget Sound. The am 2 are those from currents
measured in the Narrows and Admiralty Inlet by Cannon et al.
(1979), Puget Sound’s Main Basin by Cannon and Laird (1972),
Elliott Bay by Larson (30 day Aanderaa current meter record,
unpublished), Port Townsend by Crown Zellerbach, Inc. (unpub-
lished), and in the Harbor at site C94. The ac 2 corresponding
409

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11111111111111111 iiiiiiiiiii_
.3 • . l
VARIANCE :. . ..
I I I I I I I I I j u 1 • I I I 1
I 0’
Figure VIII-6. PLAN VIEW OF TME VARIANCE OF CURRENT METER RECORDS
TAKEN BETWEEN 0-20 M DEPTH. SHA 9 ED AREA DENOTES
VARIANCE OF LESS THAN 0.10 M 2 S . DASHED LINES
ARE INFERRED CONTOURS. CONTOUR INTERVAL - 0.1 M 2 S 2 .
40’
‘5,
30’
2 0
I 0’
48°
tO’
1230
26
(5’
.4Q
.21
5,
40’
48°
10’
30’
20’
5’
(230

-------
.4
SILL ZONES [ 1 i’.TN
E RS’
w
O •BB
‘IPUGET SOUND
— 1 JUAIN BASIN
PA /
>
o yA /
Ia.I LB ITO PT,
Io, i1 ,
/
(I )
‘U
IodI
/
/
/
-
COMPUTED KINETIC ENERGY (m’ s’)
Figure VIII-7. KINETIC ENERGY COMPUTED FROM TIDES VERSUS
VARIANCE FROM CURRENT METER MEASUREMENTS
KEY: Al - Admiralty Inlet
TN - Tacoma Narrows
GV - Green Point — Victoria sill
RS — Rosario Strait
BB - Bellingham Bay
PAH - Port Angeles Harbor
PT — Port Townsend
EB - Elliott Bay
A - variance data May - June 1979
B — variance data August - September 1980
411

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to the locations of the current measurements in Puget Sound
were determined from volumetrics of McLe].lan (1954) and
in the Harbor from Table 111-1. Figure VIII-7 shows that
there is an approximate correlation of am 2 and ac 2 except
for the Harbor: its measured variance is twentyfold greater
than expected for local tides. From this one can conclude
that a significant amount of kinetic energy is generated with-
in the Harbor by tidal flows immediately exterior to the Har-
bor.
The signatures of eddies within the Harbor may be evident in
the water property distributions. Figure VIII-8 shows plan
views of SSL for selected surveys from Callaway et al. (1965).
The SSL patterns show several closed contours which may be
associated with tidal eddies.
2. Eddy Induced Mean Currents
The plan view of mean currents near the water surface (0 - 5
m depth) is shown in Figure VIII-9 based on a synthesis of
historical current meter records listed in Table 1 11-A—i. The
general pattern consists of a flow seaward (westward) at mid—
channel with speeds of 20 — 40 cm s - and a counter current
adjacent to shore flowing inland (eastward) at speeds of 5 -
35 cm
The vertical section of mean flow at mid—channel has been des-
cribed for the Strait by Herlinveaux and Tu].ly (1961), Cannon
(1978), and Holbrook et al. (1980); through the San Juan Pas-
sages into the Strait of Georgia by Redfield (1950) and Waldi-
chuk (1957); and into Puget Sound by Barnes and Ebbesmeyer
(1978). These studies indicated that the mid-channel flow
consists of less saline water in surface layers flowing sea-
ward above approximately 50 in depth and oceanic water at depth
moving landward through the Strait, Admiralty Inlet, and Haro
Strait (Figure Vill-lO). This estuarine circulation is caused
412

-------
E
o 5
w O
a-
U)
0
z
Is
E
I
we
w
I
WO
25 ‘ 26 27 28 29 30
AUGUST 1963
Figure VIII-8. PLAN VIEW OF SSL (a) AND SALINITY (b) IN HARBOR ON AUGUST 30, 1963.
WIND (c) AND TIDE (d) DATA ARE SHOWN FOR 5 DAYS PRIOR TO AND INCLU-
DING THE SURVEY DATA
20’
$0.
H
Lb 2 / Yh,JI/ /L, 4 ..A/ ttAL.. 4 .JJI/ ill
c)WIND H_____
d)T IDE
Source: Callaway Ct al. 1965

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40
30’
20’
I 0’
4r
$0’
‘5’
MEAN FLOW
5’
40’
()
30’
$0’
11111111111
20’
10’
5,
123
Figure VIII-9 . PLAN VIEW OF MEAN SURFACE CURRENTS IN THE STUDY AREA
(VELOCITIES IN CM/S). A AND B REPRESENT MID-CHANNEL
FLOW; C - K REPRESENT DIVERGING, CONVERGING AND COUNTER
CURRENTS INDUCED BY TIDAL EDDIES.
1* _

-------
r
&W1 CE RICA CANNON
STRAIT OF $&* N CE FUCA
SAN &&6 N PASSAGES
STRAIT OF GEORGIA
200
400
I
I—
0
0o
0o
0
OCEAN
ENTRANCE
200
DISTANCE INLAND (km)
300
Figure Viii-1O. CROSS SECTIONAL VIEWS OF THE PUGET SOUND - STRAIT OF JUAN DE FUCA - STRAIT
OF GEORGIA SYSTEM
Source: Adapted from Ebbesmeyer and Barnes l980& Waldichuk 1957.
Lower panel: Bottom profiles from mid-channel to head of Port Angeles Harbor, Port Townsend
Bay, Bellingham Bay & Everett Harbor

-------
in large part by mixing less dense freshwater with more
dense coastal waters. The two constituents are mixed by
tides and winds; the mixture flows to sea and is replaced at
depth by an inland flow.
The net landward movement of deep oceanic water from the mouth
to head of the Strait has been substantiated using seabed
drifters by Barnes et al. (1972). They released seabed drif-
ters off the Oregon and Washington coast and recorded a sig-
nificant number of recoveries in the Strait, Puget Sound,
Rosario Strait, and the Strait of Georgia (Figure VIII-fl),
In general their observations indicate a continuous net land—
ward flow at depth from the ocean to heads of the various in-
land arms.
Vertical profiles of mean currents near the shore, in the counter
current are shown in Figure VIII—12. From surface to bottom
the flow is directed eastward. The surface speeds increase
eastward from a near zero value at the ITT Rayonie,r outfall,
to 3 - 10 cm s 1 near Ediz Hook, to 13 cm off Green Point,
to 16 - 52 cm s off Dungeness Spit. Near the bottom the
speeds also increase eastward at rates that are consistent
with those measured toward mid-channel. The net flow patterns
that arise near the two major spits can be interpreted in terms
of tidal eddies.
a. Durigeness Spit : Inspection of the measured mean currents
in Figure ViIi-9 shows that they are directed toward the tip of
Dungeness Spit. On its eastern side the mean northern flow is
induced by tidal eddy E5. On the flood tide in the lee of
Dungeness Spit tidal eddy E5 develops such that currents flow
clockwise causing northward currents along the shore. On the
ebb tide there are also northward flowing currents. Thus at
most tidal stages there are currents flowing northward toward
the tip of Dungeness Spit.
416

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.
S.. •••• • S.
S
.:‘L ‘
• .• • •
: •. • \ ‘
S ••
•: ?,&.:‘ ••.
• .. S
S • S
..
. S S
S
1241
43°
43.
t•.••.•.• . .•••••
• •:
: •‘. •
.5..... •• lb...
PACIFIC
48•
OCEAN
4 ..
Rivs n uth
0
>40m
K
No r.co .srss
50
• •_ L.._’
S HYPOTHETICAL PATHWAYS
(LINES), and APPROXIMATE RECOVERY POSITIONS (ARROW-
HEADS) OF SEABED DRIFTERS FOUND MORE THAN 100 4
FROM THEIR RELEASE POINTS (FROM BARNES ET AL. 1972)
417

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0
=
I-, I00
a.
U
0
200 I I I —
60 40 20 0 20 40 60
WESTWARD —CURRENT SPEED (cm S”) —...EASTWARD
Figure VIII-12. VERTICAL PROFILE OF CURRENT SPEEDS IN THE
NEARSHORE COUNTERCURRENT (STIPPLED) COMPARED
WITH THOSE AT MID-CHANNEL (HATCHED)
KEY: 0 = sites 7,8,9,10
& = Tollefson et al. Ti
= site NOS C8
Q= site NOS C82
•= site NOS 20
COUNTER
CURRENT
I
I MID CHANNEL
418

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The net northward flow was observed by Frisch (June 1980)
near the surface using high frequency radar. Mean currents
computed over 5½ days in July 1979 showed northward speeds
of 15 - 35 cm This result suggests that the mean currents
induced by the flood and ebb eddies may be of comparable speed.
On the northern side of Dungeness Spit the net northeastward
flow is induced by tidal eddy E12. On the flood tide currents
set toward the northeast, whereas on the ebb tide tidal eddy
E12 forms in which currents flow counterclockwise and also
northeastward along Dungeness Spit. Thus at most tidal stages
the mean flow is northeastward in the region bounded by shore
and the eddy center. The resulting net mean speed toward the
northeast is evident at sites HNOS 20 and C82.
b. Ediz Hook : Near Ediz Hook eddies develop on both flood and
ebb tides. On the flood tidal eddy E3 develops east of Ediz
Hook and induces a net northward flow across the mouth of the
Harbor in a manner similar to the development of the northward
flow east of Dungeness Spit. The mean speed of the northward
current as measured at Site T2 is approximately 3 cm s and
markedly lower than the comparable speed if 15 - 35 cm
measured near Dungeness Spit.
On the ebb a comparatively small and intense eddy develQps on
the north side of Ediz Hook and induces a net eastward flow in
a manner similar to the ebb tidal eddy north of Dungeness Spit.
The speed of this current at surface as measured just east of
Ediz Hook at site Tl is 4 cm s 1 and significantly lower than
the corresponding speed of 29 cm s 1 measured just eastward of
Dungeness Spit at site UNOS 20.
The eastward flow is also suggested by changes in shape of Ediz
Hook. Sediments enter the marine waters from the Elwha River
and shore side cliffs, and apparently are carried eastward so
419

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as to nourish Ediz Hook. Damming of the Elwha River in 1910 -
1911 and 1925 - 1928 and the construction of a water supply
line with rock covering in 1930 along the base of the cliffs
between the Elwha River and Ediz Hook resulted in approxi-
mately a 75% decrease in the sediment that feeds Ediz Hood
(U.S. Army Corps of Engineers 1971). The subsequent erosion
of the Hook suggests that the net transport of suspended sedi-
ment eastward to Ediz Hook was interrupted.
The comparatively low eastward speed measured near Ediz Hook
may be due in part to a divergence of flow. At the eastern
end of the Hook part of the mean flow continues eastward and
a fraction returns to enter the Harbor.
c. Port Angeles Harbor : FigureVIII-13 shows a plan view of
the mean speed and direction from historical current records.
Also shown are trajectories from experiments in the hydraulic
tidal model. The experiments consisted of following the tra-
jectory of a drift particle (bronze dust) released near the
Harbor’s head and along the southern shore until the particle
exited the Harbor’s mouth. The experiment was repeated ten
times at each release location and at a number of tidal ranges
where in each case the bead was released at lower—low-tide.
At all tide ranges the trajectories meandered about those shown
in Figure VIII-13.
The model experiments indicate that surface water in the southern
portion of the Harbor moves eastward and northward so as to
join the net northward flow induced at the Harbor’s mouth by
the tidal E3 described earlier. In order to satisfy continuity,
Figure VIII-13 shows a net westward flow in the northern portion
of the Harbor. -
The pattern of mean currents is consistent with the reports of
earlier investigations which were based primarily on water
420

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FIgure VIII— Plan vi of oct circvtatton La the larbor. lotatien: surface net fl s
13 (solid arrws); net fla,. at depth (daah.d arr s); neseured o ct currents
(.- ) taken by Toll.fsou et c i. (1971), wher, the ainbers indicate .pocd
(cu s1) and depth (n); trajectory of beads released in hydraulic tidal
nodal (dotted array.); A, eastward ficu north of £diz liock; 1, dtvsrgsnce
into the rbor contiaiiaga sbwe at C; D, veatward fl at depth in Earbor;
E, eddies; P oct eastward fin’ fren surf ace to botten; C, cosversnoe; I,
net fin’ .e.b ,ard near IT t dock; I, divsrs.c.; 3, L, L, M, cocntarcurrsat.
—4
421

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property distributions. Figure VIII-14 shows plan views of
mean water properties (temperature, salinity, and SSL) deter-
mined from the approximately monthly surveys of Cal].away
et al. (1966). In order to avoid bias associated with particu-
lar tidal phases the surveys were first averaged within subsets
of those occurring on ebb (9), flood (2), and slack (1) tides
and then the subset averages were themselves confined to ob-
tain overall means. Surveys during periods of significant
winds (< 10 knots; one survey) and no SSL discharge (one sur-
vey) were excluded. The resulting mean patterns appear
similar to those reported previously by USD1 (1967) and Tollef-
son et al. (1971) using different data sets and averaging pro-
cedures.
Inspection of the present water property patterns indicates that
surface water in the Harbor consists of two types. Water in
the northern half is characterized by comparatively low temp-
erature, high salinity, and low SSL; whereas the southern half
is characterized by comparatively high temperatures, low sali-
nity, and high SSL (at least prior to relocation of outfalls).
The sources for the freshwater and SSL in the southern half are
the discharges from minor creeks, municipal discharge, and pulp
mill effluent. The dispersion of these effluents results in
the patterns observed in the southern half of the Harbor. Sur-
face waters having characteristics of the northern half of the
Harbor lie exterior to the Harbor. The source water may well
be the eastward flow in the northern side of Ediz Hook.
Currents have been measured at 16 m depth in the Harbor (site
C94) and in profile near the Harbor mouth at sites Ti and T2.
Figure VIII—13 shows a plan view of the mean currents near 16 m
depth and the inferred general circulation. At the Harbor mouth
the net flow is northward at approximately 3 cm l apparently
induced by eddy £3. This current is joined by a net outflow
from the northern portion of the Harbor and continues eastward.
We speculate that the flow in the southern portion of the Harbor
is also eastward.
422

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I
[
L SURVEYS TAKEN BYCALLAWAY
(D) IN THE HARBOR SUR-
ET AL. (1965):
‘$0..’
. 107*
10.7 .
‘
— --- ,: • •.*...

-------
The circulation pattern and hydraulic model experiments sug-
gest that water is being drawn out of the Harbor by tidal
processes. Among the processes is entrainment by eddy E3,
which develops on flood tides of water from the Harbor. To
illustrate the overall tidal pumping behavior the transit time
between the Harbor head and mouth were determined from the hy-
draulic model experiment noted earlier (Figure VIII—15). Des-
pite the assumptions implicit in the model the dependence of
the transit time on tide range is evident. We conclude that
net flow in the Harbor is dependent on tidal processes.
d. Countercurrent Between the Two Spits : The temporal and
spatial extent of the countercurrent can be deduced from a’
synthesis of historical records of water properties and cur-
rents. A process that explains the observations is illustrated
by experiments using the hydraulic model.
The pulp mill effluent can be used to trace the countercurrent.
The effluent has two signatures: first is a relatively direct
measure of its concentration as expressed by the PBI; and second
is the toxicity of the effluent as expressed by the percentage
of oyster larvae abnormality. Three surveys were conducted in
which the stations were adequate to resolve the spatial patterns.
Figure VIII-16 shows contours of toxicity and PBI for the surveys.
The contours indicate a continuous current that extends to Dun-
geness Spit.
The observations in the countercurrent can be used to test for
its presence through the year. Table VIII-1 lists the dates for
the various types of observations that indicate the presence of
the countercurrent. For toxicity and SSL only data earlier than
1975 were used because afterward the major pulp mill (ITT Rayonier)
significantly altered their treatment processes. The tabula-
tion shows that evidence of the countercurrent has been observed
in most months. We conclude that the countercurrent is a reason-
ably permanent feature of the general circulation pattern in the
Strait.
424

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FLOOD TIDE RANGE (ft.)
0 1
I
E
U
LU
LU
$3 0.
0 ,
I-.
z
L0
U
OIL SPILL 3.0
:
FLOOD TIDE RANGE (m)
Figure VIII-15. RESIDENCE PERIOD ESTIMATED IN HYDRAULIC TIDAL
MODEL EXPERIMENT FROM THE TRANSIT OF BEADS WITH
REPEATING TIDE
Key: • mark bead release position
Athe residence period determined from SSL
• the transit time for oil spilled at the
Harbor mouth
(Mean and standard deviations are from ten trials
for each flood tide range)
N(PCATING AREA O
YlOC PARTIcLE TRAJECTORY
L
S.
3,
U,
. 4
LU
I-
C /,
z
0
0
3
425

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20’
I0’
I0’
to’
5’
‘5’
30’
I I I I I I
I 0’ 123°
i9u e VIIX—16 c intStCUTTSflt In tbs stiMy ar.. em traced esIng oyster bisesemy tests
of effluent tenicity. Dsta obtained ftc. surveys by Card. s11 et .1. (1977).
lotation: 1i it stipple, sst.r than S ahao 1ity; nediue stipple, eatur
th 2O ab .o 1ity; dark stipple, greater th S αemi.slity.
426

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Table VIII-1. OBSERVATIONS OF WATER PROPERTIES AND CURRENTS
INDICATING THE PRESENCE OF THE COUNTERCURRENT
Source: Paulik 1966; Cardwell et al. 1979;
National Ocean Survey — —
(see Appendix Ill—A)
Site
(48° 09 06’,
281
(op )
Water Properties
10 Site
123° 13.42’) (48° 10.24’,
Abii. PSI
( ) (o
11
123° 11.24’)
Abn.
(7.)
Currents
21 Jan. 1964
5
77
30 March 1964
17
46
18 May 1964
lOMay 1972
10
3
6
6
6
22 June 1964
13June1972
32
9
92
9
23
1
23
9 July 1964
20 July 1964
13 July 1963
24 July 1973
15 July 1974
6
19
11
24
8
66
17
51
1
12
6
9
2
1
17 Aug. 1964
27 Aug 197.
19
15
28
17
23
82
6 Sept. 1963
9
5
15-13 Oct. 1975
19 Occ.3 Nov.
1975
Site
Site
C8
C82
18 Nov. 1963
30 Nov. 1964
14
12
30
21
a
16 Dec. 1963
10
15
427

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In the study area the prevailing winds are from the west through-
out most of the year. In order to test the hypothesis that the
countercurrent is driven by winds, daily average currents in
the countercurrent at site C8 were compared with local winds
(Figure VIII-17). During most of the current meter record, the
winds were either calm or did not exceed 5 m s ; whereas the
countercurrent was reasonably steady. The correlation suggests
that the countercurrent is not a transient feature associated
with wind effect.
A characteristic of the countercurrent is an increase in along—
shore speed toward the east. Figure VIII-18 shows the mean speed
for current meter records obtained in the 0 - 5 m depth range.
The observations ‘indicate that the mean speed increases approxi-
mately linearly from near zero near the eastern end of Ediz Hook
to 35 cm s near the eastern end of Dungeness Spit. Then the
elapsed time for a water parcel to travel the distance (24 kin)
between the ends of the two spits is approximately 1.3 days.
Thus materials released near the shore between the two spits
travel quickly to Dungeness Spit.
3. Residence Period of the Harbor
A number of approaches were used in an effort to determine the
amount of time (i.e. residence period) waste materials remain
within the near surface waters of the Harbor. Field data of
SSL and an oil spill were evaluated and supplemented by experi-
ments in the hydraulic model.
a. SSL Patterns : SSL is generally concentrated in the near
surface waters and can be used as a tracer to provide an esti-
mate of the residence period for water in the Harbor. For this
computation we have assumed that the amount of SSL in the Harbor
is in a steady state so that the input of SSL always equals
losses from the Harbor. A similar approach has been employed
extensively in estuaries using freshwater as a conservative
tracer.
428

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Figure VIII-17.
WINDS (a), TIDE (b), AND CURRENTS Cc) DURING SEPTEMBER 3 -
NOVEMBER 3, 1975 AT PORT ANGELES
(The current reversal occurs on October 26, 1975 (vertical
dashed lines) as clearly shown at site NOS C83 (5 m depth))
0
‘A l
‘a
U)
z
E
I-
Sal
a
I-
E
U
a
‘a
‘a
a.
U)
I-
z
‘a
U
SEPTEMBER I 9 7 5 OCTOBER NOV.

-------
F
gito
I-
z
I d
10
C)
SITE
b)
SITE
I
_J
0. 4
Z
o 0
z
4 c13
4
I d
C-)
U
o z
(_) I d
0
C l)
ALONGSHORE DISTANCE (km)
Figure VIII-18. Alongshore variations in the countercurrent of speed (a), SSL
concentration, and frequency of abnormality (b). The alongshore
distance is reckoned from the eastern end of Ediz Hook and the
sites are shown at top of (a) and (b).
a)
TI
( J
0
0 10 20 30
Source: Paulik 1966.

-------
Derivation of residence time was performed, taking SSL decay
as a function of temperature while expanding the decay rate
function to linear terms (see Appendix VIII-A). This was accom-
plished through analysis during time periods when only the mill
within the harbor (Fibreboard) was discharging.
For a period of 15 days (August 19 - September 3 1963) SSL was
discharged only near the head of the Harbor at the Fibreboard
plant. Eleven days (August 30) after the beginning of the inter-
val SSL concentrations were measured throughout the Harbor by
Callaway et al. (1965). During this interval the discharge
rate at the Fibreboard plant was found to be 860 tons day -l
(USD1 1967). From data of Callaway et al. (1965) we deternined
that 1800 tons of SSL were contained in the Harbor on August 30.
Substituting these values and time decay constant T = 12 days
into eq. (5) in Appendix ViII-A we obtain a residence period
of T = 2.7 days. It should be noted that the mean water temp-
erature on August 30 was approximately 12°c and close to the temp-
erature on which the time constant is based.
The effect of the SSL decay on the residence period can be
determined by comparing results from eq. (1) without decay with
eq. (5) with decay (see Appendix VIII-A ). The residence period
computed with decay taken into account is 2.7 days; whereas the
period without considerir g decay is 2.1 days. Thus decay acts
to increase the residence period by 0.6 days orapproximate].y
29%. We conclude that the decay of SSL cannot be ignored in the
interpretation of the field data.
The residence period computed above may be influenced by winds.
The observations of winds at Ediz Hook showed that during each
of the three days prior to the observations on August 30 there
was a typical westerly seabreeze having speeds of 15 knots dur-
ing the afternoon. The plan view of SSL concentrations at the
surface (Figure VIII-l4) suggests that the seabreeze drove sur—
face water toward the southern shore. The overall effect would
431

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be to expel SSL from the Harbor at a faster rate than in
the absence of wind as obtained in the hydraulic model.
b. Hydraulic Model Experiments : It is interesting to
compare the particle transit time as determined in the
hydraulic model with the SSL residence period. The SSL resi-
dence period of 2.7 days occurred during a period (August 27 -
30) when the tide had a flood tide range of 5.1 feet. In con-
trast the corresponding particle residence period is 2.4 days
as shown in Figure VIII-15. Since the difference is well
within the standard deviation of the experimental results,
the SSL and bead residence periods may be considered as equiva-
lent. However the model experiments were conducted using a
different tidal curve than occurred in the field. The tide
in the model consisted of two high and two low waters per day;
whereas the tide that occurred during the SSL computations
consisted of a single high and low water per day. The effect
of different tide curves on the residence period remains
undetermined.
The experiments indicate that the residence period decreases
to approximately 1.3 days for the tide ranges of six - eight
feet and 0.3 days for ranges in excess of nine feet. This period
indicates that material inputs are exchanged over the length of
the Harbor in about a tidal cycle. Some evidence of this move-
ment is found in observations of an oil spill.
On May 13, 1979 an oil spill occurred near the Harbor mouth at
lower-low-water during a period of spring tides (Figure VIII-19).
Aerial photographs were taken about a day later at mid-stage
during a major flood tide. The winds during this period were
mostly calm with occasional reports as high as 3 m 1• The
photographs showed that slicks and sheens had spread to the head
of the Harbor in 1.2 days. Although not conclusive this data
does support the model result at higher tide ranges.
432

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Figure VIII—19.
• •;.
ELWHAR -
2
0
)
MAY 1979
DISPERSION OF OIL FROM A SPILL (X) ON MAY 13,
AS OBSERVED (STIPPLED) MAY 14, 1979.
RIP = rip line associated with Elwh.a River discharge
13 14 15
433
1979
LL

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The field data and model experiments suggest that the
residence period in the Harbor depends on tide range. The
available field data correspond to tidal ranges of 5.1 feet
(SSL) and 8.5 feet (oil slick); whereas the mean range is
4.2 feet. The particle residence period at the mean range is
3.5 days. Assuming that the shape observed in the model is
representative of field conditions, then in the absence of
wind the typical residence period is approximately four days.
c. Deeper Water : Thus far our considerations of residence
period have pertained to water near the surface. Fifty percent
of the SSL occurs in depths shallower than three meters, and
the depth of the experimental particle corresponds to a proto-
type depth of at most a few meters. Although there are insuf-
ficient data to quantify the period at greater depths there are
some data to indicate some upper limits to the period.
Some idea of the Harbor’s response may be obtained by contrast-
ing the seasonal cycles of various water properties outside
and inside the Harbor. Observations of temperature, salinity,
dissolved oxygen, and SSL were taken by Callaway et al. (1965)
at a dozen locations in the Harbor and at a reference station
approximately two kilometers north of Ediz Hook at approximately
one month intervals from February 1963 to January 1964. These
data were averaged at the observation depth; the averages near
surface and bottom in the Harbor were compared with those at
corresponding depths at the reference station (Figure VIII-20).
The water properties inside the Harbor appear to closely follow
that in the Strait. We conclude that the residence period of
the Harbor is significantly less than the month interval between
surveys.
In another experiment using the hydraulic tidal model the Harbor
was filled with water soluble dye (India Ink). After a week’s
434

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30
_ 2-
U -
0
-
U i -
-
I-
Ui
U i
I—
8-
32
I-
Z3Q
C,)
32
0.5
a
wO.5-
>-
0
0.3
MONTHS
Figure VIII-20. SEASONAL CYCLES AT SURFACE AND 40 M DEPTH OF
TEMPERATURE, SALINITY, DENSITY AND D.O. IN
PORT ANGELES HARBOR (SOLID) AND AT A REFERENCE
STATION (DASHED) 2 KM NORTH OF EDIZ HOOK
Source: Callaway et al. 1965
J ‘ F’ M 1 A 1 M 1 J 1 J ‘A’ S ‘0 1 N’ D’J
23
a
24
,- 25-
U,
2
U i 24
25
J’F’M’A’M’J’J’A’S’O’N’D’J
J ‘F’M’A’M’J’J’A’S’O’N’D’J
SURFACE
40m
4
40m
I
/ SURFA
,‘• 4 0 m
“I ,. ; > . .
.4-.
435

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time in the model most dye evident to the unaided eye had
escaped the Harbor. All remaining dye was located in the
Harbor’s deepest section below sill depth.
The seasonal cycles and model experiment indicate that an
upper limit to the residence period in the deeper water is on
the order of weeks.
4. Dispersion of Pulpmill Effluent
The dispersion of pulp mu], effluent depends to a large extent
on the horizontal and vertical location of the point of dis-
charge. The diffusers at the end of the discharge pipe provide
an initial dilution on the order of 100:1 on horizontal scales
of the order of 10 2 m. At intermediate horizontal scales of
102 — 1O 4 in the dispersion is a strong function of horizontal
position. In the far field the effluent is quite diluted but
enters the general estuarine circulation at mid—channel and thus
is carried to sea and to the inland arms including Puget
Sound and the Strait of Georgia.
a. Vertical Distribution : Discrete samples of SSL in verti-
cal profiles have been obtained by Callaway et a].. (1965) in
the Harbor approximately monthly from September 1963 to January
1964. Outside of the Harbor SSL samples have been obtained
primarily near the water surface (e.g. Cardwell & Woelke 1979).
Figure vIII-21 shows vertical profiles of SSL averaged within
winter and summer seasons. These profiles were obtained by
horizontally averaging the array of stations taken by Callaway
et al. (1965). Analysis of the mean profiles shows that 0.5 of
the SSL was contained in the upper 3 m depth and that 0.9 was
contained shallower than 15 in depth.
Since these measurements were made, the ITT Rayonier effluent
and its discharge location have changed due to the installation
436

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a
E
=
I-
Figure VIII—21.
SSL. (ppm)
SEASONALLY AVERAGED VERTICAL PROFILES OF THE
MEAN CONCENTRATION (LEFT) AND CUMULATIVE
AMOUNT (RIGHT) OF SPENT SULFITE LIQUOR IN PORT
ANGELES HARBOR
Source: Ebbesmeyer et al. 1979; Ca].laway et al.
1965 —
KEY: CZ — Crown Zellerbach Corp.
F l - Fibreboard, Inc.
ITT — ITT Rayonier. Inc.
Inset shows locations of sampling stations and
locations and percentages of SSL input.
CUMULATIVE SSL (tone X 1O )
3 4 5
437

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of primary treatment and recovery of SSL. No observations
of Crown Ze].lerbach effluent are available. The vertical
location of the effluent discharged through ITT Rayonier’s
percent deepwater diffuser has been estimated using both a
numerical model and field measurements. Numerical models
have been developed which predict the vertical location and
dilution of an effluent plume discharged from a diffuser. A
model developed by Teeter and Baumgartner (1979) was applied
to ITT Rayonier’s effluent as discharged through its present
deepwater diffuser. Assuming currents over the diffuser are
greater than 3 cm s 1 the plume rises to the water surface
according to that model.
Recent measurements of ITT Rayonier’s effluent plume were taken
by the EPA to calibrate the earlier numerical estimates.
These data were taken using a fluoronteter to determine percent
light transmittance through a water sample taken inside the
effluent plume versus a sample of undiluted mill effluent drawn
from within the mill. Observers in a Cessna 172 airplane dir-
ected the sampling boat to stations within a visible plume.
Water from several depths was sampled. The results of these
studies indicate the effluent was concentrated between surface
and 10 m depth (Table IV-8) (Shea 1979). Other measurements
of the effluent taken in conjunction with fluorometric measure-
ments included PBI, organic carbon, nutrients (nitrogen and
phosphorus), and suspended solids. Results of these measure-
ments indicate that ITT Rayonier’s effluent lies generally above
10 in depth, though one sample at 30 in depth (Station 1) had
high levels of suspended solids due to the presence of the eff-
luent, thus indicating that PBI alone does not show the pres-
ence of some effluent fractions.
b. Intermediate Horizontal Dispersion : Previous studies have
shown that most effluent is concentrated near the sea surface.
Thus the effluent will be dispersed by the eddy, mean, and wind
driven currents described earlier.
438

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To gain insight as to dispersion by tidal eddies dye was
injected into the hydraulic tidal model. Figure VIII-22 shows
selected photographs of dye continuously released at the posi-
tions of the two mill outfalls. These photographs indicate that
the intermediate horizontal dispersion consists of numerous
filaments and patches. The historical data base consists of
arrays of a few stations rather widely spaced; comparison with
the model photographs suggests that the effluent plumes have not
been adequately sampled.
Maps of some filaments have been obtained by visual inspection
from low flying aircraft. Figure VIII-23 shows representative
configurations on selected tidal phases. These observations
were made by EHI from a single engine aircraft positioned using
an accurate ranging system (Motorola Mini Ranger III; ± 30 m
accuracy as used aboard the aircraft). These patterns show that
filaments have been visible within the Harbor, north of Ediz
Hook, and eastward to Green Point.
At intermediate horizontal scales the effluent has been observed
to be carried consistently in the countercurrent as far as the
eastern tip of Dungeness Spit (see Figures VIII-16, VIII—22).
Given the variability of the type and volume of the ITT Rayonier
effluent discharge and the limited sampling in both time and
space, computation of an average dilution from the available
data base probably is not meaningful. However it is useful to
examine the maximum abnormality recorded at stations near Dunge—
ness Spit. Table VIII-l lists the PBI and abnormalities at Sites
10 and 1]. off Dungeness Spit prior to 1975 when chemical recovery
of 85 percent of ITT Rayonier’s SSL began. Values of PBI and
abnormality as high as 32 and 92, respectively, have been
observed. These values suggest that reasonably concentrated
patches of effluent at times may reach Dungeness Spit.
Because the SSL is concentrated near the water surface, winds
undoubtedly transport the effluent over significant distances.
439

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Figure VIII-22. PHOTOGRAPHS OF DYE INJECTED INTO THE HYDRAULIC TIDAL
MODEL AT CROWN ZELLERBACH, INC. OUTFALL LOCATIONS
(A) (ADAPTED FROM EBBESMEYER ET AL. 1979)
440

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- —7; —. -- 7 - - - - T
7PP 1Ir —
. , — _
a - ! -.
S
-;. -
Figure VIII—22.
(continued)
( )
PHOTOGRAPHS OF DYE INJECTED INTO T HYDRAULIC TIDAL
MODEL AT CROWN ZELLERBACH, INC. OUTFALL LOCATIONS
(ADAPTED F M EBBESMEYER ET AL. 1979)
441

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I
RAYON I, INC. (B).
I
442

-------
/ — 00 Nt ‘
C N I £ 0
• —. • : • •_ • • - • • . I. • •••I •
zc*T:’1 r /,i
NOUNS HOURS NOuNS
Cot’
1•— _.,..i...i..:i...;. •: -.
PH Y’H
I..
NOUNS
Cod
_ : • • •. __ I. ••I•••• •,•
SLACK, EBB AND FLOOD PATTERNS OF
VIII 23.
Source: Ebbesmeyer et al. 1979
443
29
12
9’
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KEY:
— SL 1C PATTERN
— E88 AND FL
TTERN
INSETS INDICATE
OBSERVATiON T S

-------
Figure vIII-24 shows the recovery positions of 42 drift sheets
that were released in or near the Harbor. The drift sheets
consisted of thin plastic sheets weighted and reinforced so as
to ride with the surface layer of water (see Ebbesmeyer et al.
1978). The releases were made during April 23 - 29, 1978 when
winds typically reached 10 m s toward the east. Usually the
sheets were released in the morning and recovered onshore in
the evening of the same day. The recoveries indicate that SSL
can be transported by winds quickly from the Harbor to Dungeness
Spit.
c. Far Field Pathways : Some of the effluent pathways in the
far field have been demonstrated by releases of drift cards and
an oil spill. Ebbesmeyer et al. (1978) released 700 drift cards
near the mouth of the Harbor and subsequently 273 were recovered
onshore (Figure VIII-25). Of the total recoveries 3% drifted
westward of the Harbor, 65% were found from Ediz Hook to Dunge-
ness Spit, 4% in Seqium and Discovery Bays and inside Dunge-
ness Spit, 17% on the westward shores of Whidbey Island, 5%
inland of Deception Pass in Whidbey Basin, and 6% on Fidalgo,
Vancouver, and the San Juan Islands. Cox et al. (1980) found
similar distributions (Figure VIII—26). Similar pathways of
drift cards have been reported by Paninski and Charnell (1979)
although they do not give percentage recoveries by area.
The drift card recoveries indicate that pulp mill effluent dis-
charged near the Harbor and its approaches will be transported
over a wide area to the shores of the inner Strait, Puget Sound,
and the Strait of Georgia. The recoveries of drift cards on
the north and south shores of Dungeness Spit are of particular
concern because of the National Wildlife Refuge located there.
Once dispersed throughout the Inner Strait, pathways exist to
vertically mix pulp mill effluent to depth where it then enters
Puget Sound and the Strait of Georgia within the ].andward deep
estuarine return flow. This vigorous mixing of surface and bot-
tom waters occurs both over sills such as those between Green
444

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35,
25 ’
‘5,
05’
123°
35’ 25’
15’ 05’ 123
Figure VIII-24. RECOVERIES ONSHORE OF DRIFT SHEETS RELEASED
IN PORT ANGELES HARBOR EXPRESSED AS PERCENTAGE
OF 42 RECOVERIES
Source: Ebbesmeyer et al. 1978
KEY: x - launch site
• — recovery position
445

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25 durthi 24-30 April l 7$. Iot&tios: lksr.d dots, sinus rsco,sris.;
a er.4 dots, ltipla zco srtaa with ths ab.r signifying th. absr
.1 - p 4$O 31.51, 125° 37.O’W
th. Pacific Coast o( Ysscoswsr Zs1s .
446

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: .
WASHINGTON
• .• •• S. .. . •
• : • • •. .
• • • •.•.
• • •: • : •‘ . •‘.•..
• • • •. •. • :. • • ••
447
122°
2 5
23°
22°
VANCOUVER
:,SjAND.
Fig. VIII- Racovery positt.as of drift cards releas.d in th, vicinity of Port Angeles
26 during 1-2 July 1980. Notation: i.nn. k.red dots, single recoveries;
.red dots, ltipl. recoveries vith the aber signifying the ni b r
of cards rscov.r.d. On. r.coveiy is off the p at 45 28.01, 123° 53.O’V
on the Pacific Coast of Oregon.

-------
Point and Victoria and those within Admiralty Inlet, and
within constricted passages such as Deception Pass and within
the San Juan Archipelago. The tidal mixing results in num-
erous rip and frontal zones at the water surface where floatable
materials often collect (based on visual observations by the
authors from small aircraft at low altitude). These zones
often represent the convergence of two currents where one sinks
beneath the other. In the mixing process a significant amount
of surface water is refluxed downward into the lower layer that
flows inland.
In a similar pathway, pulp mill, effluent near the surface in
the turbulent sill zones may be carried by the refluxing process
to mid-depth in Puget Sound. This transport may be imagined
as following contours of equal density southward from Admiralty
Inlet. As an example a hypothetical pathway inland is shown in
Figure VIII-27. An illustrative example of this process carry-
ing oil to depth within Deception Pass has been provided by Pro-
fessor Emeritus Clifford A. Barnes (letter to the State of Wash-
ington Department of Ecology, November 26, 1974) in Appendix
VIII—B.
The flow dynamics necessary for the downwelling of oil could more
easily mix pulp mill effluent to depth. Though actual observa-
tions of downwelling in other turbulent zones within the inner
Strait do not exist, this downwelling has been studied within
Puget Sound by Ebbesmeyer and Barnes (1980). They found that
much of the freshwater entering Puget Sound and flowing seaward
at surface through Admiralty Inlet is refluxed landward to depth
into Puget Sound’s Main Basin. Though no measurements of pulp
mill effluent have been made for verification, a mechanism does
exist to mix effluent to depth.
B. WATER QUALITY
Due to the absence of any comprehensive system of water quality
monitoring stations, little geographical analysis can be accom-
plished with present data. The last time a significant number
448

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200-
• • •. . : .•. •. •• •.
$00
200
30
Figure VIII-27. PROFILE VIEW OF DENSITY (EXPRESSED IN SIGMAt
UNITS) AT MID—CHANNEL FROM THE INNER STRAIT OF
JUAN DE FUCA TO PUGET SOUND’ S MAIN BASIN
Source: Collias et al. 1974
(Heavy lines with arrowheads denote possible
pathway at depth of oil transport into Puget Sound.)
Dates: a) September 15 — 17, 1958
b) November 19 — 21, 1958
c) December 19 — 23, 1958
449
DENSITY (sigma-t)
-
a)
0
$00..
I-
a-
w
24.

-------
of stations were sampled at one time occurred in May and Novem-
ber 1972. Isocline maps of D.O. and SSL levels on these dates
are shown in Figures VIII-28 - VIII—3].. The May readings show
highest SSL readings at the north end of Port Angeles Harbor,
while DO, readings in this area are considerably lower than
surrounding areas. The lowest D.O. readings occur along the
Port Angeles shoreline at the southern end of the Harbor. This
may indicate confounding influences from municipal sewage or
sludge beds. The November data are more closely correlated, with
highest SSL and lowest D.O. values occurring east of ITT Rayonier
along the shoreline.
Time sequence analyses can be carried out at only a few stations
using post—1970 data. Station PAHOO3 has the most continuous
and recent monitoring history, although even this has frequent
gaps. In particular D.O. readings for this station are scatter-
ed especially during the period 1971 — 1973 (Figures VIII-32,
VIII—33)
Time correlations of sharp SSL rises and D.O. depressions can
be seen from this data. A SSL rise from 80 PBI to over 500 PBI
occurred in January and February 1969. D.O. was 7.5 mg/I. in
February and dropped to near 6 mg/i in March, indicating a pos-
sible retention or time delay effect from the BOD of the wastes.
A second sharp rise in October 1969 to roughly 130 PBI corres-
ponds to a D.O. drop from over 12 mg/i to less than 5 mg/i.
During July 1970, another sharp SSL rise from 10 to 50 PBI cor-
responds to a sharp D.O. drop from over 10.5 mg/i to less than
4.5 mg/i. However an SSL increase in January and February 1970
from 50 to 200 PBI corresponds to a D.O. decrease from 7 to 6
mg/i, a drop of only 1 mg/i. In 1977 a sharp SSL spike in July
and August reached only 15 PBI but corresponded to a drop in
D.O. levels of nearly 6 mg/i, while an earlier D.O. rise occur-
red at a time when SSL levels were stable below 1 PBI (May
1977). It is clear from this data that D.O. is usually depres-
sed by high SSL levels, but that D.O. can show significant vari-
ations without being tied to SSL. The confounding influences of
450

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Figure VIII-28. ISOCLINE MAP OF D.O. CONCENTRATIONS, MAY 4, 1972
Source: STORET December 12, 1978

-------
Figure VIII-29. ISOCLINE MAP OF SSL CONCENTRATIONS, MAY 4, 1972
Source: STORET December 12, 1978

-------
Figure VIII-30. ISOCLINE MAP OF D.O. CONCENTRATIONS, NOVEMBER 1, 1972
Source: STORET December 12, 1978

-------
Figure VIII-31. ISOCLINE MAP OF SSL CONCENTRATIONS, NOVEMBER 1, 1972
Source: STORET December 12, 1978
Ui

-------
4* r.
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_v
: :i:
! ‘.111
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•!
• 4.4.
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.1..
Ff
—:
::
H-
Figure ViiI-32. D.O. READINGS FOR STORET STATION PAHOO3
Source: STORET 12/12/78
1967 — 1977
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1973
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1ISO
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-------
1978
1968 1909 1910 1911 1912 1973 1974 1975 1970 1977 1979
Figure ViII—33. SSL READINGS FOR STORET STATION PAHOO3 1967 - 1978
Source: STORET 12/12/78
E
-J
U)
U)
1980

-------
water temperature and diurnal variation confuse the data to
a significant extent. While water temperature effects can
be factored out by utilizing percent saturation instead of
D.C., diurnal variation has never been measured at Port Ange-
les. Monitoring times (time of day) from month to month tend
to be somewhat random. Correlations between D.C., SSL and
flood and ebb tidal stages were attempted; however the data
proved too fragmented on this basis to provide accurate isoclines,
even during well monitored historical periods.
The same kind of effects can be seen by examining surface D.O.
levels in some of the more comprehensive short-term water quali-
ty studies (USD1 1970; EPA 1972 a, b; Fagergren 1976). Fitting
lines to the raw data scattergraphs of surface D.C. vs. SSL
(Figure VIII-34 — VIII—37, Table VIII—2), one obtains rather
consistent slopes and D.O. intercept values (excepting the first
1972 study). SSL intercept values vary considerably, which is
not unexpected since the curve is probably logarithmic rather
than linear at high values of SSL. The r 2 values appear reason-
able given the fact that D.O. can be expected to vary indepen-
dently at low SSL values.
This type of analysis shows that D.0. and SSL are correlated and,
inasmuch as pulp mill effluent is represented by the rather non-
specific Pearl—Benson test in Port Angeles Harbor, demonstrates
periodic oxygen depletion as a result of pulp mill wastes, ex-
tending at least into 1976.
Basically, water quality monitoring data at Port Angeles Harbor
has been infrequent, scattered and haphazard, based on variations
in agency programs and monitoring requirements. The weak data
base permits no analysis of most of the more sophisticated para-
meters (nitrogen, phosphorus, solids etc.) which might lend in-
sight into the relationships between pollutants and biological
457

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75 100 125 150
SSL mg/I P81
SURFACE SSL AND D.O. LINEAR REGRESSION LINE (1970)
(Derived from USD1 1970)
0
a
7
S. C
.
—
S.C S .5
1•
I — S
e G
&I
S
.
..4
uI z
•
&s
tz
S.t
S
S.C S
S t -
S.C
S
S.
S
p
S
.
&
“.-___
b. _
0 . 25
Figure VIII—34.
175 200
22

-------
SSL mg/I P81
Figure VIII-35. SURFACE SSL AND D.O. LINEAR REGRESSICN LINE (1972)
(Derived from EPA 1972)
—
I
0
a

-------
8SL mg/I PBI
Figure VIII-36. SURFACE SSL AND D.O. LINEAR REGRESSION LINE (1972)
(Derived from EPA 1972)

-------
SSL mg/I
Figure VIII-37. SURFACE SSL AND D.O. LINEAR REGRESSION LINE (1976)
(Derived from Fagergren 1976)
E
0
0

-------
Table VIII—2. SURFACE SSL AND D.O. LINEAR REGRESSION
(Information for Figures VIII-34 — VIII—37)
Study
Slope
r 2
(D.O.)
y—intercept
(SSL)
x—intercept
USD1 1970
—.01
.48
6.57
1240.54
EPA 1972a
—.0008
.19
7.90
9027.15
EPA 1972b
—.01.
.77
6.24
433.27
Eagergren 1976
—.02
.33
6.2
358.59
462

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activity. The nearly complete lack of present data coupled with
the temporally scattered nature of past observations make.further
correlations from historical data very difficult and often inac-
curate.
Water quality sampling conducted by EPA during June 1979 also
revealed only a few new parameter relationships. Dilution mea—
surements revealed a rapid near-plume dilution, followed by a
much smaller and more gradual dilution and dispersion once the
plume reached near-surface waters. In general, the analytical
methods for most parameters were not sensitive enough during
the rough weather conditions to show variations.
Biological oxygen demand correlated fairly well with effluent
presence as measured by PBI. Organic carbon content varied
with PBI also but in a seemingly nonlinear manner, with a range
of 1.6 - 2.4 DOC corresponding to 5-15 ppm PBI. Additionally
DOC was high at a station near the outfall whose high PBI was
not recorded. This suggests strongly that the pulp effluent,
upon reaching the surface, is both patchy in its distribution
and is separated into components. While SSL may be confined
primarily to the surface layer, other components, high in car-
bon and other solids may exist at lower levels which are not
picked out by standard SSL tests for PBI. This observation
is also borne out by the high solids reading obtained at 30 me-
ters depth, and by orthophosphate levels at Station 1.
It is clear that a definite possibility exists that the plume
separates into distinct components while in the nearfield
region, and that certain of these components may travel in the
subsurface waters, or precipitate out onto bottom sediments.
Unfortunately, neither laboratory (separation and settling ex-
periments) nor field (detailed subsurface and sediment sampling)
studies have been carried out to investigate this phenomenon.
It is important to note that the separation of the plume into
463

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components implies the possibilities that 1) toxic components
may be present with little or no detectable SSL and 2) that
toxic components may be carried by subsurface currents to areas
much different than those indicated by surface current analysis.
C. TOXICITY
1. Effluent Toxicity
Effluent from the ITT Rayonier dissolving pulp, sulfite-process
mill was sampled (Cardwell et al. 1977b) on August 18, 1975 by
taking grabs of treated (after SSL incineration) and untreated
wastes from the di ester (outfall 003A) and mixed wastewaters
from extended outfall 007. On August 25, 1975 24-hour composites
of effluents from outfalls 003A and 007 were obtained. The latter
samples reflected largely the SSL incineration treatment which had
been “off-line” for an estimated 10% of the time with only 75%
(rather than the normal 85%) of the liquor being burned.
Pulpmill effluents were treated by aeration for 16 to 20 hours
at 2°C and neutralized to pH of 7.6 to 7.9 with 1.0 N reagent
sodium hydroxide. The rationale for these manipulations was to
remove variables and sources of error which would obscure the
relationships between PBI and the response of Pacific oyster larvae.
The toxicity of ITT Rayonier effluents varied with waste treat-
ment, time and duration of sample collection and the biological
response criterion. Untreated wastes were usually more toxic
than treated wastes, and wastes from outfall 003A were more toxic
than those from 007 (Table VIII-3). Treatment of 003A wastes
resulted in a 300% decrease in effects on abnormal shell devel-
opment and an 81% decrease in effects on mortality. Treated
effluent from outfall 007 actually was more (20%) toxic in terms
of abnormality, but 88% less toxic in terms of the LC5O. Even
with incineration of 85% of the solids, wastes from 003A were
3 to 5 times more toxic than those from 007. Although greater
concentrations of treated wastes were required to adversely
affect larvae, waste toxicity calculated as a function of PBI
was essentially equivalent to that of untreated wastes.
464

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Table ViiI-3. COMPARISON OF TOXICITY RESPONSES BETWEEN PACIFIC
OYSTER LARVAE AND RAINBOW TROUT FINGERLINGS IN
VARIOUS EFFLUENTS TESTED DURING 1975 AND 1976
Source: Cardwell et al. 1977b
EFFLUENT
PACIFIC OYSTER LARVAE
FINGERLING & RAINBOW
TROUTb
EC5O
LCSO
as PBI
mg/i
as % as PBI
Effluent mg/i
as %
Effluent
96-MR LC5O
% Effluent
19
a,
August 1975
003A untreated
003A treated
31
28
0.015 7,500
0.062 2,300
3.5
5.5
7
> 9
25
007 untreated
007 treated
a,
August 1975
92
75
0.38 3,850
0.31 4,250
10.0
17.5
25
< 18
003A treated
007 treated
23
50
<0.0222 1,430
0.31 1,130
1.25
5.25
9
36
15
June 1976
007
14 ( 2 _ 26 )C
0.12(.01—.23)
27
July 1976
007
1.9(17—20)
0.i.6(.14—.l8)
25.5(22—27)
18
August 1976
007
25(23—26)
0.17(.17—.18)
23.8(17.4—32.6)
2
December 1976
007
10(10—11)
0.22(.22—.23)
25.2(23.1—27.5)
8 low—pit
liquor (SSL)
17(16—18)
0.00099(.00094—.011)
1.02(0.8 —1.28)
a conf. limits were not calculated and median responses are approximations
b Static tests in soft freshwater (Folsom & Denison 1976)
C 95% confidence limits
d Effluent samples treated by aeration and pH neutralization
465

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There were great differential effects of these effluents on
shell development and mortality. The amount of effluent re-
quired to kill larvae was from 17 to more than 200 times great-
er than that causing abnormal development. The August 25,
1975 tests essentially confirmed these results, except that 24—
hour composites of both wastes were more toxic. The EC5O for
003A was 14 times lower than 007, while the LC5O was 4 times
lower. Although LC5O values based on PBI were comparable be-
tween wastes, the EC5O for 003A was less than half (<23 mg/i
PBI) that for 007 (50 mg/i PSI).
Static toxicity tests of the same effluents were conducted by
Folsom and Denison (1976) using soft freshwater and fingerling
(<50 mm TL) rainbow trout. Relative to the abnormality criterion
for larval oysters, the trout were more tolerant (58 to 467
times) of the effluents; with respect to the mortality criterion
trout were only slightly more tolerant (0 to 7 times). Patterns
in toxicity were comparable between oysters and trout.
Considerable variation in chemical content of the effluent be-
tween treated and untreated wastes was found (see Table VIII-4),
Untreated effluent 003A possessed greater organic content
than untreated wastes from effluent 007. Treatment of 003A
resulted in about 79% reduction in total solids and PHI, an 81%
reduction in furfural content, and 86 to 88% reductions in total
ammonia, BOD and COD. However there was no appreciable change
in the highly acid character of this waste stream. Sulfite waste
liquor incineration had relatively little effect on the com-
position of outfall 007 because some liquor was being discharged
in this effluent at the time of sampling. Both wastes were
similar in total solids, D.O., pH, NH 4 , and furfural contents,
although treated wastes had somewhat lower SOD, COD, formic and
acetic acids.
The 24-hour composite of treatedwastes on August 25, 1975 were
different from those obtained earlier. This was evident for 003A,
466

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Table VIII-4. CHEMICAL COMPOSITION OF ITT RAYONIER PULP
MILL EFFLUENTS
Source: Cardwe].1 et al. 1976; Cardwell et al. 1977b
003A
8/19/75
003A
tests
007
007
8/26/7’5
003A
tests
007
Chemical parameters untreated
treated
untreated
treated
treated
treated
Total solids. % 2.15 0.46 0.24 0.24 1.40 0.25
Total susupended solids
mg/2.C
P31, mg/i 215,000 46,000 24,000 24,000 140,000 26,000
C
Color
D.O., mg/i 3.4 6.4 5.6 6.1 7.5 7.6
pH 2.52 2.68 2.90 2.64 2.35 4.08
Spec. Cond. uxnhos/cm 6,000 2,600 2,000 1,600 4,700 1,400
Ammonia, mg/i 748 94 15 15 361 3].
Residual chlorine mg/i N.D.b N.D. N.D. N.D. a
T.0.C., mg/R.
B.O.D., mg/iC 5,925 819 152 280 10,170 492
C.0.D., mg/iC 27,727 3,204 838 1,293 17,888 1636
Furfural, mg/iC 125 24 3 4 108 N.D.
5—methyl furfural, 10 N.D. N.D. M.D. M.D.
mg/ic
Furfural alcohol, mg/I.
Formic acid, mg/ic 208 129 32 71 390 264
Acetic acid, mg/iC 438 135 39 75 377 252
To 1 mercury, mg/i 0.010 O.Oll
Organic mercury, mg/i 0.01
Total chromium 0.014 — 0.023
Hexavalent chromium N.D.
Zinc 0.084 — 0.i
Copper 0.007 — 0.025
Lead 0.044 — 0.062
Cadium 0.004 — 0.007
Nickel. M.D. — 0.006
Magnesium
Not measured Folsom and Denison (1976) and units bounded by parentheses
Not detected Ranges for the two effluents. Single values represent identical
e readings.
mg/i
467

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Table VIII-4. continued, page 2
Total solids, %
Total suspended solids
mg/L
PBI, mg/i
C
Color
D.O., mg/i
pH
Spec. Cond., umhos/cm
Axzmtonia, mg/i
Residual chlorine, mg/i
a
T.O.C., mg/9.
C
B.O.D., mg/i
C.O.D., mg/iC
Furfural, mg/iC
5-methyl fuzfurai , mg/iC
Furfural alcohol, mg/i
Formic acid, mg/iC
Acetic acid, mg/iC
Total mercury, mg/i
Organic mercury, mg/i
Total chromium
Hexavalent chromium
Zinc
Copper
Lead
Cadium
Nickel
Magnesium
a Not measured
b Not detected
375
3,450
(0.03)
(2.87)
.(— 14.2)
(1,010)
750
2,250
20
1,975,000
(1,348,000)
1.6
1.5(2.3)
27,500
3,060
44,000(48,000)
325,000
600
6/15/76
007
7/27/76
007
8/18/76
007
12/2/76
007
Blow—pit
Chemical Parameters
L .quor (SSL)
0.25 021 ( 2200 )e 027 ( 2600 )e
0.24
13.7
(33)
(21)
(166.7)
14,700 12,000
i4,600(10,200) 9,200(6120)
(2,280)
7.8
6.2
6.0
5.1
3.65
3.20(3.25)
3.4(3.36)
3.8(3.45)
1,650
1,780
2,010
1,800
65 55
555 (650)
4,100
15
43 22
(—7.1)
900
2,400
23
N.D.
N.D.
130
140
(<0.1)
(0.008)
(0.34)
(0.05)
(<0.01)
M.D.
N.D.
N.D.
N.D.
N.D.
M.D.
73
105
320
51
115
3,100
(<0.1)
(<0.1)
(<0.01)
(0.04)
(0.74)
(1.0)
(0.95)
(0.4)
(0.7)
(0.03)
(0.12)
(0.3)
(<0.01)
(<0.01)
(<0.01)
(1.6)
(1.8)
(0.04)
(3.01)
Folsom and Denison (1976) and units bounded by parenthesis
Ranges for the two effluents. Single values represent identical
readings.
e mg/L
468

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which had over 3 times as much total solids, 4 times higher
NH 4 concentration and over 2 times more BOD than its treated
equivalent sample one week earlier. In contrast, treated
waste from effluent 007 was similar to those of August 19
(Table VIII—4
Extended outfall 007 was sampled on June 15, July 27, August
18 and December 2, 1976 and tested within 24 hours of collec-
tion. Effluent samples tested in 1976 were not altered by
aeration or pH adjustment. Effluent from outfall 007 was rela-
tively constant in acute toxicity between June 15 and December 2,
1976 (Table VIII—3). Median EC5O’s ranged from 0.12 to 0.22%
ef fluent and from 10 to 25 mg/i PBI. This effluent was much
less toxic than a sample of the digester liquor (EC5O of
0.00099% effluent) that supplied the bulk of the toxic substance
discharged by this mill prior to 1977. Most of outfall 007’s
toxicity was derived apparently from P81 substances since the
toxicity of both 007 and the liquor were similar when based
upon PBI (Table VIII-3).
Several of the samples of outfall 007 were concurrently tested
with rainbow trout fry and the ninety-six hour LC5O’s for the
various wastes were virtually identical (23.8 — 25.5% effluent)
(Table VIII—3). Much higher concentrations (115 to 159 fold)
of outfall 007 were required to kill, rainbow trout fry within
96 hours than were necessary to elicit abnormal development in
oyster larvae in 48 hours. An even greater disparity in toxic-
ity was evident between the two species with respect to digester
liquor; oyster larvae were 1,000 times more sensitive than trout.
2. Receiving Water Toxicity (Nearfield )
Additional toxicity testing of ITT Rayonier mill effluent and
receiving waters was conducted using the oyster larvae bioassay
during June 6, 7 and 8, 1979 (Cuminins et a).. 1980). During
this testing it was necessary to use a partially stripped egg
suspension because a sufficient number of eggs could not be
469

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obtained through induced natural spawning. Possibly as a
result most control mortalities exceeded the limits prescribed
for definitive testing. However it has not been clearly est-
ablished that elevated control level abnormality and mortality
necessarily indicates an increased sensitivity to toxicants
(Cardwell et a].. 1977a). Consequently, the relatively high con-
trol larval responses were not considered to invalidate the re—
suits (Cuznmins et a].. 1980). Net larval abnormality and mor-
tality values which compensate for high control mortality were
calculated as recommended by Cardwell and Woelke (1979).
Tests of the final effluents collected June 6 and 7 exhibited
rather constant, low—level larval abnormality at calculated PBI
concentrations of c2 mg/i and <5 mg/i, respectively. At P31
levels greater than these, larval abnormality increased rapidly,
with almost 100 percent abnormality being observed at 22.4 mg/i
PBI (June 6) and 51.5 mg/i P31 (June 7). These PBI concentration—
larval response relationships are very similar to those des-
cribed by others for Pacific oyster larvae (USD1 1967; Woelke
1972)
Graphic estimates of the effluent concentrations causing 50 per-
cent larval abnormality in 48 hours (48-hour EC5O’s) were made
using the method of Litchfield and Wilcoxon (1949). Based on
these estimates, the range of 48—hour EC5O’s characterizing the
effluents June 6 and 7 was 0.17 — 0.23 percent effluent and
11.9 — 21.2 mg/i PBI. It is significant that these toxicity
estimates were almost identical to the range of 48-hour EC5O
values measured by Cardwell et al. (1977b) when conducting Paci-
fic oyster larvae bioassays on ITT Rayonier effluents collected
from outfall 007 between June 15 and December 26, 1976. The
range of EC5O’s reported by Cardwell et a].. (1977b) was 0.12 -
0.22 percent effluent and 10 — 25 mg/l PSI.
The similarity in the toxicity as well as in some of the chemi-
cal properties of the effluents collected in 1976 and 1979 sug-
gests little change in the toxicity of the ITT Rayonier effluent
since 1976.
470

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Although based on only a few observations, larval abnormality
tended to increase rapidly with increasing PBI levels. Sur-
face waters collected from Station 9, about 13 miles east of
outfall No. 007 on June 8, yielded 38.8 percent abnormality in
the presence of 18.0 mg/i PBI (Table VIII—5}. Larval abnorma].i-
ties of 96.6 percent and 100 percent were observed in surface
waters collected from Station 1, approximately 0.5 miles east
of the outfall on June 7 and 8. These waters, collected immedi-
ately east of the submarine diffuser contained 59 mg/i and 66
mg/i PBI, respectively, and were the most toxic samples collected.
It is of interest to note that the PBI concentration-larval
response relationship observed in the receiving waters was
essentially the same as that measured in the final pulp mill
effluents. This similarity suggests that final effluents from
the ITT Rayonier facility were a major source of the toxicity
detected in marine receiving waters near Port Angeles Harbor
in June 1979.
The toxicity data collected by Cuinmins et al. (1980) has been
tabulated with similar data developed byCardwell and Woelke (1979)
to show the changes which have occurred since 1972 (Table VIII-5).
High toxicity and PBI concentrations were common along the nine
miles from the Tip of Ediz Hook to the Base of Dungeness Spit
until 1975, when ITT Rayonier began incineration of up to 85% of
the mill effluent. Once incineration was implemented the sam-
pling grid utilized by the Washington State Department of Fishe-
ries became less effective because it became necessary to sample
much closer to the diffuser outfall to detect toxic effects.
However routine monitoring in 1978 did show a 100% abnormal res-
ponse at the diffuser outfall but depending on the precise sample
of water collected and daily changes in mill operation, very
low toxicity was found during other years. The stations sampled
by Cummins et al. (1980) indicate that a smaller plume of toxic
water from the diffuser is detectable for a distance of about
2.75 miles to the east (Table VIII—5).
471

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Tab .e VIII-5. MEAN PERCENT ABNORMAL DEVELOPMENT (MAXIMUM VALUE PER TIME AND DEPTH) OF
PACIFIC OYSTER LARVAE WITH ASSOCIATED PBI CONCENTRATIONS (mg/i) UP AND
DOWNSTREAM FROM ITT RAYONIER OUTFALL NO. 007 WITH APPROXIMATE DISTANCE
OF EACH STATION FROM EFFLUENT SOURCE
STATION
Year
11
3—0705
10
31—0007
1
3
13
6
7 9 4 8 5
31—0004
31—0022
03—3305
03—3306
] 972 a
595
98.35
91.56
74.36
8.82
5.73
(0)
(74)
(1980)
(29)
(10)
(6)
1973 a
44.34
100.0
100.0
100.0
59.32
1.41
(2)
(1220)
(21)
(38)
(26)
(5)
1974 a
40.68
97.87
100.0
10.52
28.08
81.56
(1)
(26)
(10)
(23)
(15)
(23)
1975 a
2.75
2.80
3.89
1.48
4.17
2.73
(0)
(5)
(19)
(1)
(3)
(1)
1976 a
0.51
0.00
1.44
3.80
1.12
(1)
(2)
(4)
(1)
(0)
1977 a
0.08
1.88
0.76
0.0
(1)
(0)
(17)
(0)
1978 a
0.00
100.0
(0)
(126)
1979 b
2.4
3.6
100.0
9.3
1.5
6.1
4.8 38.8 18.7 6.7 14.7
(<1.0)
(4.0)
(66.0)
(5.0)
(10.0)
(1.0)
(1.0)(18.0) (6.0) (3.0)(13.0)
1
0
0.5
0.75
0.9
1.0
1.1 1.3 1.5 2.6 2.75
3.75
6.2
8.0
Location
Tip of
Outfall
Off
Of f
Base of
Ediz
Morse
Green
Dungeness
Hook
Creek
Point
Approximate
Distance from Outfall 007 (miles)
SQU1Ce; Cardwell and Woelke 1979
b Cummins ct al. 1980

-------
The improvement in the quality of the receiving waters which
occurred in 1976 (Cardwell et al. 1977b) has continued with
little change to the present. The overall quality of the
waters sampled in 1979 was considered to be reasonably good.
Over 90% of the samples bioassayed by Cuininins et al. (1980)
met Woelke’s (1972) Proposed Marine Receiving Water Quality
Criterion ( 20 percent larval abnormality) for waters support-
ing fish or shellfish reproduction, rearing or harvesting;
however these bioassays were collected during a period when
weather and wave action favored a rapid breakup and dilution
of the effluent plume.
3. Receiving Water Toxicity (Farfield )
Receiving waters from 27 stations have been sainp].ed and bio—
assayed in the Port Angeles region (Freshwater Bay east to
Dungeness Spit) since 1962 (Figure VIII-38). Only surface sam-
ples were collected prior to 1971; however the results demon-
strated that large areas of this region were highly toxic to
oyster larvae from year to year (Cardwell and Woelke 1979).
Beginning in 1972 both surface and subsurface (0, 6, 12 and 18 m
depths) water samples were collected and bioassayed usually
during the month of August. The period 1972 to 1978 is reviewed
here since it represents the period in question before, during
and after waste treatment was initiated at the ITT Rayonier mill.
Larval Pacific oysters commonly develop abnormally within 48
hours in sulfite pulp mill effluent (SME) concentrations less
than either 50 mg/l PBI or 0.05 to 0.2% effluent (USD1 1967;
Woelke 1960). Concentrations of SME causing 50% abnormal develop-
ment in larvae of horse clam ( Tresus capax and T. nutta].li) ,
native littleneck clam ( Protothaca staminea ) and geoduck ( Panope
generosa ) are quite similar to oyster larvae (Schink and Woelke
1973). Abnormal shell development is a sublethal response which
evidence indicates ultimately leads to death. Woelke (1960)
found that abnormal Olympia oyster ( Ostrea lurida)larvae did not
473

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I - ,
12 f3O
12120’
STRAIT OF JUAN
12 J’1O’
DE FUCA
12 OO’
0 t5 3
4.5 5
miles
•‘
24
23
Protection
‘0
0 •
Figure Viii-38 LOCATION OF SAMPLING STATIONS AND PULPMILL EFFLUENT DIS-
CHARGES IN THE PORT ANGELES REGION
)
Source: Cardwe].]. et al. 1977b

-------
metamorphose to juveniles when exposed continuously to sub-
lethal concentrations of SIi]E. Salmonids appear much more
tolerant to SME than bivalve larvae. The 96-hour LC5O ranging
from 2000 to 2400 mg/i PBI has been reported for juvenile At-
lantic salmon ( Salnio salar ) (Wilson 1972) and from 0.7 to 2.2%
for juvenile rainbow trout ( Salmo gairdneri ) exposed to various
types of SME (Rosehart et a].. 1974). Bivalve mollusc larvae
are therefore about 40 or 50 times more sensitive than juvenile
rainbow trout. A similar difference was reported between lar-
vae of Pacific oyster (48—hour EC5O = 50 mg/l PBI) and larval
Pacific herring and spotshrimp (48—hour EC5O = >4000 mg/i PBI)
with tests of a sodium salt of lignosulfonic acid, common in
SSL (Cardwell et al. 1977a).
Since Crown Zellerbach closed its sulfite mill in 1964 and
relocated major process waste discharges to the Strait in 1967,
state research programs have found no important effects on the
receiving water quality (Cardwel]. et al. 1977 b). The ITT Ray-
onier plant had a rated pulp production capacity of 550 air-
dry metric tons/day and generally discharged 117,300 m 3 of waste-
water daily, 84% via outfall 007 and 16% via 003A (Figure VIII—39).
Following installation of primary treatment outfall 003A carried
most of the SSL and contributed 66% of the 268,000 kg BOD sew-
ered daily (490 kg BOD/metric ton pulp). A major change in ef-
fluent treatment occurred in August 1975, just prior to the 1975
samples collected from the receiving waters, when incineration
of 85% of the SSL production began (see Chapter II for details).
During 1976, prior to sampling the receiving water in August,
the effluent stream from 003A was combined in 007.
The toxicity of outfall 007 to oyster larvae was greater in
1976 (mean of 0.17% effluent) than in 1975 (0.31% effluent)
(Cardwell et al. 1976). The approximately two—fold increase in
toxicity probably represents the addition of chiefly non-volatile
condensates from the SSL recovery system and pulp wash waters
that were previously discharged via outfall 003A. This increase
475

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Figure VIII-39. LOCATIONS SELECTED FROM THOSE SAMPLED FROM 1964 TO 1976 IN WEST CENTRAL
PUGET SOUND FOR ANALYSIS OF VARIATION IN TOXICITY TO OYSTER LARVAE AS A
FUNCTION OF THE LOCATION AND DATE OF SAMPLING AS WELL AS COVARIATE EFFECTS
Source: Cardwell and Woelke 1979
West Central
Puget Sound
STRAIT OF JUAN
03-3307
03-1418
3 O’03-42 j 03-3304
343 pp
03-3310
I ‘YMPIC

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in the acute toxicity of 007 due to the 003A contribution was
approximately the amount expected.
Toxicity maps of the receiving water in the Port Angeles region
(Figures VIII-40, viii—41) showed that toxicity was greatest in
1973 and 1974, when more than 50% of the larvae developed abnor-
mally in water from an area of more than 27 km 2 (Cardwell et al.
l977a). In 1972 about 15 km 2 of water was similarly toxic. An
improvement in the quality of the receiving water occurred in
1975 when incineration of 85% of the SSL reduced BOD loading
by about 50% (Figure VIII—42). About 0.7 km 2 of water within
this region was highly toxic in 1975, representing a decline of
97% from the 1973 - 1974 period. Essentially zero receiving
water toxicity was found during the 1976 survey (Figure VIII—41).
a low level (cli percent abnormal development) of recurring water
toxicity was found in inner Port Angeles Harbor and near the ITT
Rayonier mill during the 1977 survey. A single toxicity response
in 1978 was reported from directly over the submarine outfall 007
where 100 percent abnormal development occurred (Figure VIII—41).
Statistical analysis of some of the data collected in the Port
Angeles region was conducted by Cardwell and Woelke (1979).
The long-term, annual variation in receiving water quality from
1.964 to 1976 for 13 of the locations sampled (Figure vIii—39)
was examined.
Visual inspection of the data revealed that receiving water
effects on abnormality and mortality of larvae varied consider-
ably between locations and to a lesser extent between years.
Larval mortality seemed more variable than abnormality. Most of
the variability in abnormality between locations and years seemed
due to the PBI content of the waters (i.e. larval responses in-
creased in conjunction with higher PBI concentrations, indica-
tive of the presence of sulfite pulp mill effluents). Salinities
rarely fell below 20 ppt and thus did not have a confounding
effect on the results. The age of the seawater samples at the
time of testing increased from 120 to 240 minutes prior to 1972,
477

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TOXICITY MAPS - PORT ANGELES AREA
(Cardwel]. et a].. 1977a)
478

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RECEIVING WATER TOXICITY TO OYSTER
LARVAE IN THE PORT ANGELES REGION
reVIIi 41.
1976 — 1978
Source: Cardwell et al. 1977b;
CardweU. 7i Wueike 1979
479

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8 T
a
In
6. 6002
1
2
D Ψ0
I-
U
0 400
0
o
a.
000 200
02
0 I I I I 0
1972 74 76 78
YEAR
Figure VIII-42. PULP PRODUCTION AND BOD LOADING VIA OUTFALL
007 OF ITT RAYONIER 1 - WEEK PRIOR TO EACH
RECEIVING INVESTIGATION
Source: Cardwe].1 et al. 1977b
480

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and to 300 to 500 minutes thereafter. The latter reflected
the lag time associated with performance of larger studies.
Analysis of variance (ANOV) tests (Cardwell and Woelke 1979)
were utilized to determine the importance of these factors on
the larval responses and to discriminate variation in toxicity
between locations and years. Larval abnormality was affected
significantly (p 0.001) by both factors, the interaction be-
tween the factors, and by the three covariates (salinity, PBI,
and age of seawater). Of the total variation in larval abnor-
mality, 44% was explained by sampling location, while the inter-
action between sampling date and location accounted for an addi-
tional 42%. The date and covariate effects had minor, though
important, singular roles. The results of the ANOV using larval
mortality as the criterion variable followed a pattern similar
to that for abnormality. Sampling data and location effects
were almost equally important explaining 22% and 20%, respec-
tively, of the total variation. The most important covariate
was PBI, explaining 2% of the total variation, while the age
of seawater had no significant influence on mortality.
Oyster and clam larvae frequently do not develop abnormally or
die at comparable concentrations of the same toxicant. Res-
ponses vary considerably in sensitivity to different toxicants
with untreated sulfite pulp mill effluent; they differ in sen-
sitivity by about 2 orders of magnitude. Mortality is a much
less sensitive response.
When the data were ordered in terms of the relative effect of
particular stations and dates on oyster larvae abnormality and
mortality, the rankings were considerably different. Locations
contiguous to the ITT Rayonier pulpinill or along the normal east-
ward path of effluent flow caused the greatest larval abnormality;
those in Seguini and Discovery Bays and other locations where the
waste had undergone substantial dilution were least toxic. Con-
versely 1 larvae mortality was highest in Sequim and Discovery
481

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Bays and actually varied inversely with distance from Port
Angeles Harbor. This is partly suspected to be due to natural
toxins in the water produced by blooms of “red tide.”
Analysis of station 03—0705 (at the tip of Ediz Hook) indicated
significantly higher toxicity (p 0.001) in 1966, 1969 and
1970 than samples collected in other years. Samples collected
in 1967 were significantly lower in toxicity than those collect-
ed in 1966, 1969 and 1970, but significantly higher than those
collected in 1964, 1968 and 1971 — 1976. The absence of appre-
ciable toxicity at this station from 1971 — 1976 is believed
partially due to ITT Rayonier’s use of an extended submarine
diffuser commencing September 20, 1972 to sewer some of its
wastes, and sewerage of all wastes via this diffuser between
the 1 .975 and 1976 WDF investigations. The 85% reduction in the
volume of wastes by incineration which began in 1975 no doubt
contributed to this improved trend in recent years. The changes
in waste disposal siting by this mill sought to provide better
effluent dilution and reduce the degree of pollution in Port
Angeles Harbor. Waste distribution patterns peculiar to each
sampling date accounted for variations observed in other years.
Even though the toxicity of the receiving water varied signifi-
cantly from one year to the next, the same sampling locations
demonstrated a similar general toxicity or lack thereof from
year to year.
D. BIOLOGICAL AND ECOLOGICAL EFFECTS
As demonstrated in Chapter VI, there is a substantial amount
of biological inventory information in Port Angeles Harbor and
the adjacent Strait. For certain organisms, abundance data is
also present; however the geographical and spatial distribution
of this data is patchy. Where data exists over most of the
study area or over an appreciable number of years, the methodo—
logies at different sites or times are often dissimilar. Thus,
for most organism groups, quantitative analysis leading to a
482

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good understanding of the ecological dynamics and the relation-
ship to pulp mill effluent are difficult or impossible. There-
fore, in this section, we will rely on knowledge of the dis-
persion of effluent, water quality and effluent toxicity develo-
ped earlier in this chapter to develop qualitative or semi—quan-
titative analysis of biotic effects. This will be done first
for each organism group, followed by a brief analysis at the
ecosystem level.
1. Phytoplankton and Other Marine Plants
The major phytoplankton groups in the Study area are diatoms.
Although many species are present, most of the biomass and
productivity is concentrated. Only data for number of cells
(abundance) tend to be available (as opposed to biomass); however
biomass data from NTPC (Table VI-3) shows that 5 - 6 species
tend to strongly dominate the total population, at least during
the winter and spring seasons. The data of Chester et al. (1978)
support this conclusion; as in 1976 one species ( Skeletonema
costatum ) alone made up 65 percent of the total phytoplankton
abundance. This concentration on a limited number of species
implies that the system may be highly sensitive to shifts in
physical or chemical parameters. This is particularly true of
pulp effluent since vertical distribution tends to concentrate
SSL fractions in near-surface waters (see Chapter IV) which are
also preferred phytoplankton locations.
A sense of this instability can be gained by analysis of phyto—
plankton seasonality. Figures VI—2 and VI-3 show that total
diatom concentrations may shift by nearly three orders of mag-
nitude (1000 times) within a 1 — 2 month period. These drastic
changes are typically part of normal growth and decay cycles in
which the sun’s energy is rapidly fixed by plankton and supplied
to the biological system to support reproductivity and growth
of higher organisms. The timing of these cycles and the parti-
cular species which undergo increases are of potentially critical
483

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importance to the animal organisms which use phytoplankton as
a food supply. Sudden increases (termed “algal blooms”) of
phytoplankton which are unusable as food (i.e. certain blue—
green algae) could potentially limit food supply for fish and
shellfish, deplete oxygen or even cause toxic contamination
(i.e. red tide organisms). These effects are well documented
in the general biological literature.
That pulpmill effluents can affect algal productivity and
physiology has been demonstrated by Eloranta and Eloranta (1974)
and others (see discussion in Chapter VII). In addition, 1979
field studies showed chlorophyll depletion as a function of
distance from the ITT Rayonier outfall. There is therefore
strong evidence that algal growth, productivity and inter-
specific competition could be affected by effluents. The imp-
lications of case—specific effects at Port Angeles are unknown
due to lack of study as are potential chronic long—term effects.
However the demonstration of effects in the literature coupled
with field correlations suggest that effluent which has not
received secondary treatment has considerable potential for
damaging marine ecosystems at the level of primary plant pro-
duction. This may apply to Iviacrophytes, wetland plants and
seagrasses as well as phytoplankton; however such effects will
be conjectural until physiological studies are conducted on
these organisms.
2. Zooplankton
Due to their small size zooplankton are probably the least well
documented class of organisms in the Strait. They occur through-
out the marine and tributary waters and provide the link between
primary producers and the higher organisms. The abundance data
of Chester et al. (1978) and Simenstad et al. (1979) show that
copepods (specifically harpacticoid copepods) form the most abun-
dant group. Although pulpmill effluents have been shown to de-
trimentally affect certain small invertebrates (amphipods) and
484

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adult forms which have planktonic larvae, copepods and most
other zooplankton have not been studied. Gaxmnarid amphipods
have been found to be affected by pulpmill effluents
(see Chapter V and Table VII-5). These organisms were found
by Simenstad et al. (1979) to contribute a large fraction of
nearshore zooplankton biomass and are identified as being
important prey organisms for nearshore fish (Simenstad et al.
1980)
Icthyoplankton present along the shoreline form the early life
stages of many recreationally and commercially valuable marine
fish. Planktonic forms of many non-salmonid marine fish are
found in the area. Physiologically, these early life stages
are much more susceptible to physical/chemical changes than
are their adult forms. Since they have no locomotive abilities,
these organisms are carried by the nearshore currents and cannot
move away from effluents or other pollutants.
Based on present data no correlations of pulp effluent effects
on icthyoplanktOn survival can be established. However pulp
effluents are known to affect the adult forms of many of the
icthyoplankton. Icthyoplankton are of small size, lack inde-
pendant mobility and are generally more sensitive to environ-
mental changes than their adult forms. It is likely that phy-
siological studies would show effects of effluent on these or-
ganisms.
In particular, areas east of Port Angeles are spawning areas
for halibut. Larval herring are present in the spring as
are sand lance (see Section VI.E.2d). Surf smelt also spawn
in Dun eness Bay, although in lesser abundance. Icthyoplankton
of all of these marine species may be affected by pulpmil].
effluent from Port Angeles. Since salmonids spawn in the tri-
butary streams, their larval forms are not susceptible to
pollution in the marine waters.
485

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3. Shellfish
Shellfish occupy the intertidal and subtidal habitats of the
Harbor and much of the Strait shoreline, both east and west
of Port Angeles. Areas of particular concentration are the
Harbor itself, Green Point and Dungeness Bay. Hardshel]. clams
are present in significant quantities in the vicinity of the
ITT Rayonier deep water diffuser (see Figure VI-7), as well as
to the east in shoreline areas off Bagley and Siebert Creeks.
Geoducks are also present in the latter area and both outside
and inside Dungeness Spit. All of these areas are within the
typical flood tide effluent path of Crown Ze].].erbach and ITT
Rayonier effluents (see Section VIII.A).
Although shellfish typically have planktonic larvae (see Sec-
tion VIII.D.2), the adult stages of clams and oysters are bottom
dwelling filter feeders which lack mobility. As filter feeders,
these organisms strain large volumes of water in order to ob-
tain food and are therefore known to be highly susceptible to
physical (via clogging) or toxic chemical pollutants. Shell-
fish often tend to accumulate toxic substances and their high
sensitivity to pulpmil]. effluent has prompted their use in bio-
assays (see Chapter V).
Oceanographic studies of effluent dispersion have demonstrated
that the pulpmil]. effluent paths near Port Angeles often lie
along the shoreline (see Section VIII.A). In addition, water
quality studies conducted during 1979 (see Chapter IV) have
suggested that toxic effluent constituents and large amounts of
suspended solids from the ITT Rayonier deepwater diffuser may
remain in bottom waters or precipitate out onto bottom sediments.
Such precipitation and/or bottom transport could potentially
have detrimental effects on shellfish, particularly those in
the effluent path (along the shoreline east of Port Angeles, or
the areas near Ediz Hook). Due to the immobility, i ost shell-
fish exposed to such pollution will be unable to relocate once
486

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they have passed out of their planktonic larval state.
Shrimp which remain motile in their adult state would have
the ability to remove themselves from high effluent areas.
4. Other Marine Invertebrates
Benthic organisms are largely dependant on the physical and
chemical properties of the substrate which forms their habi-
tat. Studies of areas near pulpmill outfalls at Port Angeles
during the 1960’s showed that sludge beds and areas exposed to
high effluent concentrations were damaging to benthic organisms.
The Puget Sound Enforcement Conference results (USD1 1967)
showed that benthic fauna were substantially damaged by both
the substrate and the volatile solids in untreated effluent
residue (Figure VIII—43). Treatment process changes through the
mid—1970’s reduced the amount of solids emitted by the mills;
however general toxicity was not substantially reduced by pri-
mary treatment (see Chapter V). In fact, English (1972) found
percent volatile solids to have increased in many benthic samples
(see Table VI—21).
Recent studies have not been made to determine the residual
state of the Crown Zellerbach or ITT Rayonier sludge beds in
Port Angeles Harbor. Neither have conditions near the present
deepwater diffusers been analysed near either mill. Water
quality tests carried out by EPA, NEC and EHI in 1979, indicate,
however, that solid fractions are highest in the deeper water
layers and that not all toxic components correlate with the SSL
fractions (which tend to remain at nearsurface levels). Pulp
effluents which settle or are carried by deep currents may be
affecting subtida]. benthic invertebrates near the diffusers or
at distances depending on those currents.
Lighter fractions (such as SSL) of the effluent tend to stay in
near—surface waters. These are often brought near or on—shore
487

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I .
ii.
12 I
t
I .
I
12.
I
I
II • •
• •
‘
•• ••
‘4
.4
S. S %
‘ 4
. 4 S
I
S .4
‘ 4
. 4
S. S .\
.
2
I I
S — — —
I. a Tr— — o a a
10 20 3 3 40 U SO TO SO
% vaNtlis
Solids
Figure VIII—43. Correlations between volatile solids and benthic organisms in
bottom samples
Source: USD1 1967

-------
by the dynamics of the countercurrent (see Section VIII.A)
east of Port Angeles and will affect shallow subtidal and inter-
tidal benthic invertebrates under certain current conditions.
Crown Zellerbach effluents (during flood tide) and ITT Rayonier
effluents (during ebb tide) would also influence subtidal
and intertidal habitats along Ediz Hook.
Goodwin and Shaul (1978) have shown that pea gravel is one of
the most preferred substrate types in this area for clams.
Analysis of clam densities shows that population levels are near-
ly zero for all areas containing wood chips, wood debris or
sludge which do not contain pea gravel (average density 0.3
organisms/meter squared). Comparing only those stations con-
taining a pea gravel substrate, Port Angeles had an average den-
sity of 2.53 organisms/rn 2 while Green Point averaged 2.79 organ-
isms/rn 2 . Areas at Port Angeles containing wood chips, wood
debris and/or fibrous sludge (including stations both with and
without pea gravel) averaged 0.4 organisms/rn 2 . These data there-
fore indicate that pea gravel improves clam substrate even in
areas with wood or sludge and that areas of identical substrate
yield somewhat higher densities at Green Point than at Port
Angeles. However, the differences are not significant statis-
tically since standard deviations of the data sets are on the
order of the values themselves (Table VIII-6).
5. Fish
Anadrornoua Fish: Anadromous fish spend only the late juvenile
and adult portions of their lifetime in marine waters. During
the period after juveniles have left the freshwater streams,
they often utilize nearshore migration routes, utilizing
copepods, amphipods and other zooplankton which
are most abundant in the nutrient enriched nearshore waters.
Adult forms are more widely ranging, except when they seek out
tributaries for spawning. Pulprnill effluents can be expected
to affect juvenile fish in nearshore areas where the counter—
489

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Table VIII-6
CLAM DENSITIES (PER M 2 ) IN SEDINENTS NEAR PORT
ANGELES
Source: Goodwin & Shaul 1978
I
Substrate

Wood Chios, Wood Debris
or Fibrous Sludge
Pea Gravel
No.
No.
iLocation
Stations S.D.
Stations
S.D.
!Port Angeles
20 0.4 1.01
15 2.53
2.50
Green Point
0 N.D. N.D.
39 2.79
2.83
Key:
— Mean Value
S.D. — Standard Deviation
490

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current keeps pulp effluents entrained during flood tides
east of Port Angeles and during ebb tides near Ediz Hook
and west toward the Elwha. Concentrations of juvenile fish
are typically highest in nursery or rearing habitat such
as that provided by eelgrass or algal beds along Ediz Hook or
at the mouth of Mqrse Creek. The Dungeness National Wildlife
Refuge also provides sheltered habitat and large numbers of
salmonids originating from the Dungeness River utilize this
area as rearing habitat. That sa].monids are sensitive to pulp—
mill effluents has been demonstrated by bioassays with trout
and salmon at both Crown Zellerbach and ITT Rayonier (see Chap-
ter V). In addition, bioassay results improved significantly
following installation of primary treatment. It is probable
that effects would be similar in marine waters, although no
recent in situ (live—box) tests have been performed.
Seasonal natural escapements from the rivers and creeks near
Port Angeles (Table VI-.I-2) have been tabulated for the past
two decades for pink and coho salmon. There is clearly consi-
derable natural variability. Escapement levels have been low
since the 1960’s although some increases occurred in 1971 -
1973. Although the year 1979 produced the highest recent es-
capement of pink salmon, the numbers are not sufficiently dif-
ferent from past years to identify effects of secondary treat-
ment at Crown Ze].lerbach or ITT Rayonier as definite causitive
factors in the improvement. Coho salmon levels have maintained
relative stability in recent years.
Marine Fish: The bulk of the marine fish data results from
beach seine data on random dates during the 1960’s (Stein and
Dennison 1966) and from recent monthly studies by Cross et al.
(1978). These authors have derived seasonal and annual totals
of fish density at various Strait of Juan de Fuca locations in-
cluding Morse Creek and Dungeness Spit (Appendix VI-K ). The
data, however, show opposite results during 1976 — 1977 versus
1977 — 1978. During the first survey, densities at Morse Creek
were 0.11 fish/rn 2 , exactly half of the 0.22 fish/rn 2 found at
491

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Dungeness, while during 1977 - 1978 densities were considerably
lower in both areas with 0.04 fish/rn 2 at Dungeness and 0.08
fish/rn 2 at Morse Creek. It should be noted here also that stan-
dard deviations were as large or larger than the data values
themselves.
6. Wildlife
Marine Mammal-s: Data on marine maitunals, except seals, is
seldom quantitative, and if quantitative, is highly inaccurate
due to the high mobility of the animals. Seal data fluctuates
highly with location and is not available over any extended
period of time. It is clear, however, that most seals within
the zone of potential effluent effects will be found in the
Dungeness National Wildlife Refuge. Seals and whales in other
areas will be only infrequent and sporadic visitors. The most
likely pulpmill effects on these organisms will result from food
chain transfers rather than from direct physiological damage.
Marine Birds: Major marine bird concentrations in thestudy area
occur west of the Harbor; however concentrated resting and feed-
ing areas also occur at Green Point and Dungeness Bay. As with
marine mammals, effects of pulpmill effluents are most likely
to result from food chain transfers. Potential effects on water-
fowl are not known to have been studied.
7. Ecological Dynamics
Only two main ecological factors can be related directly to
effects from pulpmill effluent at Port Angeles: productivity
loss and direct physiological damage to consumer organisms.
From these, food chain transfer effects and influence on eco—
system diversity and stability can be hypothesized in some
detail; however sampling directed at determining the extent of
these latter effects has never been conducted.
492

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Primary productivity as measured by chlorophyll concentration
is lessened by a factor of four or more in the vicinity of the
ITT Rayonier outfall. Crown Zellerbach effluent effects on
chlorophyll have not been measured.
This acute effect on productivity may be accompanied by more
subtle chronic damage to phytoplankton which drift through the
effluent plume. The effect is greatest in the zone a few meters
below the surface where both SSL concentrations and phytoplank-
ton density tend to be highest.
Bioassays carried out in the receiving waters coupled to
numerous laboratory studies with marine organisms show that
many marine animals experienced toxicity damage as a result
of exposure to Crown Zellerbach and ITT Rayonier effluents.
More recent bioassay tests have shown a significant reduction
in toxicity since the introduction of secondary treatment (see
Chapter V). Based on the food web structure of the ecosystem
these toxic effects are potentially transferrable to other
organisms, thus possibly directly or indirectly affecting nearly
all organisms at the upper trophic levels with concurrent dam-
age to ecosystem diversity or stability.
493

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Features of Juan de Fuca Strait.” Journal of the Fisheries
Research Board of Canada ]8:1027-1071.
Holbrook, J.R., R.D. Muench, and G.A. Cannon. 1980. “Seasonal
Observations of Low-frequency Atmospheric Forcing in the
Strait of Juan de Fuca.” IN: Fjord Oceanography (H.J.
Freeland, D.M. Folmer, and CD. Levings, eds.), Plenum Press,
New York. pp. 305—318.
Larson. Unpublished Data. See Ebbesmeyer, et. al., 1980.
Litchfield, J.T., Jr. and F. Wilcoxson. 1949. “A Simplified
Method of Evaluating Dose-Effect Experiments.” Journal
of Pharmacology and Experimental Therapeutics. Vol. 96
#2. pp. 99—113.
496

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McLellan, P.M. 1954. An Area and Volume Study of Puget Sound .
University of Washington Department of Oceanography,
Technical Report No. 21. 39pp.
National Ocean Survey. Unpublished Data. U.S. Department of
Commerce, National Oceanic and Atmospheric Administration.
Rockville, Maryland.
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.
Paulik, G.J. 1966. Final Statistical Summary Report on Larval
Bioassay Study . University of Washington Department of
Fisheries, MS., 32 pp.
Redfield, A.C. 1950. “Note on the Circulation of a Deep
Estuary - the Juan de Fuca - Georgia Straits.” IN:
Proceedings Colloquiin on Flushing of Estuaries . Woods
Hole Oceanographic Institution, 175-177.
Rosehart, R.G., G.W. Osborn, and R. Mettinen. 1974. “Origins
of Toxicity in Suiphite 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 . Final Report for Grant 1BO5ODOJ
to EPA, Naragannsett, R.I.
Simenstad, C.A., B .S. Miller, C.F. Nyblade, K. Thornburgh, and
L.J. Bledsoe. 1979. Food Web Relationships of North
Puget Sound and the Strait of Juan de Fuca . Prepared for
MESA Puget Sound Project, NOAA.
Simenstad, C.A., B.S. Miller, C.F. Nyblade, K. Thornburgh and
L.J. Bledsoe. 1980. “Food Web Relationships of Northern
Puget Sound and the Strait of Juan de Fuca.” Environmental
Protection Agency. Washington, D.C.
Shea, G.B. 1979. Water Quality Analysis, June 1979, Port
Angeles and Vicinity . U.S. Department of Justice/U.S.
Environmental Protection Agency, Region, X. Seattle,
Washington. 13 pp.
STORET. 1978. Unpublished Data. U.S. Environmental Protection
Agency, Region X. Seattle, Washington.
Teeter, A.M. and D.J. Baumgartner. 1979. Prediction of Initial
Dilution for Municipal Ocean Discharges . EPA — Corvallis
ERL, Pub. 043. Corvallis, Oregon.
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Tollefson, R., J.G. Denison, and E. Tokar. 1971. “Outfall
Location Studies - Port Angeles, Washington.” ITT Rayonier
Olympic Research Division Report No. HlO:1-3 Case 1230—16,
Project 119:116 dated 30 August 1971.
U.S. Army Corps of Engineers. 1971. Report on Survey of Ediz
Hook for Beach Erosion and Related Purposes, Port Angeles,
Washin ton . Main Report, Parts 1 and 2, U.S. Army Corps
of Engineers, Seattle District.
United States Department of the Interior. 1967. Pollutional
Effects of Pulp and Paper Mill Wastes in Puget Sound .
U.S. Department of the Interior, Federal Water Pollution
Control Administration, Northwest Regional Office,
Portland, Oregon. Washington State Pollution Control
Commission, Olympia, Washington. 474 pp.
United States Department of the Interior. 1970. Port
Angeles Washington Water Quality Survey . Survey No. 1.
Office of Technical Programs, Technical Assistance and
Investigation.
United States Environmental Protection Agency 1972a. Port
Angeles, Washington Water Quality Survey No. 2 . Surveillance
and Analysis Division, Region X. Seattle, Washington.
United States Environmental Protection Agency. 1972b. Port
Angeles, Washington Water Quality Survey No. 3 . Surveillance
and Analysis Division, Region X. Seattle, Washington.
Waldichuck, M. 1957. “Physical Oceanography of the Strait of
Georgia, British Columbia.” Journal of the Fisheries
Research Board of Canada 14:321—486.
Wilson, R.C.H. 1972. “Acute Toxicity of Spent Sulfite Liquor
to Atlantic Salmon ( Salnio salar).” Journal of the Fisheries
Research Board of Canada . 29:1225-1228.
Woelke, C.E. 1960. Effects of Sulfite Waste Liquor on the
Normal Development of Pacific Oyster (Crassostrea gigas)
Larvae . Res. Bull. No. 6 State of Washington Department
of Fisheries. Olympia, Washington.
Woelke, C.E. 1972. Development of a Receiving Water Quality
Bioassay Criterion Based on the 48 Hr. Pacific Oyster
( Crassostrea gigas) Embryo . Washington Department of
Fisheries Technical Report No. 9. 93 pp.
498

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IX. CONCLUSIONS
The data and analyses presented in previous chapters have shown
that the Crown Zellerbach and ITT Rayonier pulpmills at Port
Angeles, Washington have presently and historically emitted
waste effluents which travel considerable distances in the
receiving waters, degrade water quality, cause toxicity to
aquatic organisms and in other ways are harmful to the aquatic
ecosystem. Secondary treatment of these wastes has been shown
to reduce toxicity and improve water quality, although the high
variability of the effluent (especially in the case of ITT Ray—
onier) often makes pre — post treatment comparisons difficult.
After the shutdown of Crown Zellerbach’s sulfite mill in the
early 1960’s, the mill has discharged mechanical pulp wastes
first to Port Angeles Harbor (hereafter Harbor), and later to
the Strait of Juan de Fuca (hereafter Strait). Diversion of
wastes to the Strait reduced many of the severe water quality
problems in the eastern harbor. During the 1977 — 1978 period,
under permit requirements to improve effluent quality the mill
installed the Ventron Process (to eliminate zinc), therrnomechani-
cal pulping, and (in 1978) secondary treatment. These three
changes are believed to have improved water quality and substan-
tially reduced effluent toxicity and ecological damage, although
the documentation for Crown Zellerbach is scant.
The Crown Zellerbach mill was over 14 months late in complying
with the requirements to install secondary treatment. In addi-
tion, the mill had 16 known Biochemical Oxygen Demand (BOD) vio-
lations (1975 — 1980), 5 known (average) Total Suspended Solids
(TSS) violations (1977 — 1980) and 13 known pH violations (1977 -
1980) during recent years, including the non—compliance period.
On September 10, 1980, a settlement was reached between the
U.S. Government and Crown Zellerbach Corporation stipulating that
Crown Zellerbach would pay $195,000 to compensate for civil
penalties claims filed by the government due to the mill’s de—
layed compliance with secondary treatment requirements.
499

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ITT Rayonier first discharged effluent to the Harbor, and,
after 1972, to the Strait via a submerged diffuser outfall.
The effluent content varies considerably due to the variations
in the sulfite process which are product-dependant. This
variation has considerably complicated documentation of water
quality violations and toxicity. In December 1975 when spent
sulfite liquor (SSL) recovery was installed, the amount of
SSL in the effluent was considerably reduced, although SSL
compliance was not achieved until February 1976.
Secondary treatment or its equivelant was required by July 1,
1977 but was not installed until September 1979. Compliance
was not achieved until October 1979, twenty seven months after
the required date. During the past 5 years, including the non-
compliance period, ITT Rayonier has had over 2,000 recorded
spills or violations of permit requirements. Following a long
and complicated legal history, the U.S. Government is now seek-
ing civil penalties for the two and a quarter years during which
the mill was out of compliance.
Waters of the Harbor and Strait are classified as A and AA waters,
respectively. Fourteen industries and other point sources
presently or historically have contributed effluents to these
waters. The largest point source in the area is ITT Rayonier
(41.8 mgd) followed by Crown Zellerbach (6.74 mgd) (excluding
the river water flow—through systems of the salmon channels on
the Dungeness and Elwha Rivers). Port Angeles Sewage Treatment
Plant is the third largest point source with 2.5 mgd. Using 1980
data, ITT Rayonier contributes 81 percent of the total effluent
load, while Crown Ze].lerbach contributes 13 percent.
Crown Zellerbach’s secondary treatment has considerably lowered
BOD and has decreased TSS slightly. Although permit violations
still occur for these parameters, they are now less frequent than
prior to secondary treatment. The Ventron Process has virtually
500

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eliminated problems resulting from zinc. ITT Rayonier with
secondary treatment has also lowered BOD significantly, al-
though violations have continued into 1980. During the period
of non—compliance, BOD was violated on a nearly continuous
basis. TSS was not monitored during the non-compliance period,
but currently violations continue to occur.
Both Crown Zellerbach and ITT Rayonier effluent contain many
naturally occurring substances which are concentrated or chemical-
ly altered into toxic organic compounds and concentrations dur-
ing the pulping process. ITT Rayonier effluent is known to con-
tain at least 11 compounds which have been identified as toxic
by the general literature, while Crown Zellerbach has monitored
only one such compound. In addition, toxic compounds including
slime control compounds, bleach, and other additives form toxic
substances in the effluent streams. A review of pilot plant
data shows that secondary treatment reduces the concentrations
of most of these toxic compounds considerably, although a few
increase due to chemical interactions. Inorganic compounds, .such
as cadmium, chromium, copper, lead, mercury, zinc, chloride and
sulfite are also known to be toxic and are often oxidized to
less toxic forms or are retained by the secondary treatment pro-
cess.
After discharge to the receiving waters, effluent from the mills
is subject to rapid initial dilution in the nearfie].d plume. The
dilution ratio is roughly 1:100 as calculated from water measure-
ments. Light fractions, including SSL, rise to the surface
or near—surface waters and are acted upon by surface currents.
Although little is known about the denser fractions, it is known
that some separation exists and that these portions of the eff-
luent are acted upon by mid—depth or bottom currents which may
be considerably different than surface currents. Although it
is unlikely that deep sludge beds (such as those caused by the
mills during the 1960’s) are recurring near present outfalls,
nearfield water quality sampling has revealed the possibility
that considerable amounts of solids are found in the deeper waters
501

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and may be deposited in bottom sediments or carried to unknown
locations by bottom currents.
Dispersal of the effluent plumes in the farfield is governed
by nearshore currents and eddies, driven mainly by tidal energy.
The typical plume pathways have been documented through ocean-
ographic monitoring and calculations, and through use of a
tidal hydraulic model of the ea. The plumes from both mills
lie in a generally easterly direction at flood tide. The Crown
Zellerbach plume parallels the outside o’f Ediz Hook, possibly
merging or paralleling the ITT Rayonier plume east of the Hook.
The ITT Rayonier effluent passes along the nearshore zone east
to Dungeness Spit or beyond. On ebb tides, Crown Zellerbach
effluent tends to move west toward the E].wha River, while the
ITT Rayonier effluent generally curls around the outside of Ediz
Hook often with some portion of the effluent entering Port
Angeles Harbor.
Dilution in the farfield is much slower than the nearfield dilu-
tion which occurs as the effluent rises from the diffuser. Far-
field dilution is typically in the range of 1:5 to 1:10 over
the first few miles of effluent transport. Total dilution of
ITT Rayonier in-plant effluent at Green Point (approximately 5
miles east of the diffuser) was measured to range from 1:330 to
1:1000. It is probable, due to the higher energy environment
west of Ediz Hook, that Crown Zellerbach dilution is somewhat
higher. In the plumes, effluent tends to be concentrated in
small patches which move together with the currents resulting
in a well defined plume path for distances of several miles.
Effluents from both mills therefore tend to remain in a con-
centrated, slowly spreading plume in the nearshore zone, in the
vicinity of significant sublittoral biological habitats. The
eddy patterns present in this zone tend to drive effluents on-
shore, affecting intertidal habitats as well.
502

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Examination of available water quality data shows that direct
correlations exist between spent sulfite liquor (SSL) and
depressions of dissolved oxygen (D.C.) levels. The numerical
relationship between the two parameters varies between different
studies. Most of these studies involve ITT Rayonier and Port
Angeles Harbor. Little data exists near the Crown Zellerbach
outfall, making numerical correlations of effluent concentrations
with D.C. impossible.
Water quality tests made by the U.S. Environmental Protection
Agency (EPA) prior to ITT Rayonier’s installation of secondary
treatment showed elevated levels of dissolved organic carbon
(DCC), BOD and depressed levels of chlorophyll a to be associated
with mill effluent. BOD and DOC were correlated in most cases
with increased SSL. Chlorophyll depression was correlated with
proximity to the ITT Rayonier submerged diffuser outfall. In
addition, total solids content at deeper stations seemed high,
indicating that not all effluent fractions rise to the surface.
Toxicity testing has been conducted by the mills with in-plant
effluent and through receiving water bioassays. In—plant test-
ing was generally conducted by mill personnel, whereas receiving
water bioassays were typically conducted by state and federal
agencies (Washington Department of Fisheries (WDF) and EPA),
either alone or in cooperation with the pulpmills.
In—plant toxicity tests from both mills show significant dif-
ferences in toxic response before and after secondary treatment.
Crown Zellerbach tests prior to secondary treatment had LC5O
values at or below 10% effluent concentration for all testse
Immediately following operation of secondary treatment the LC5O
value rose to the required 65% effluent concentration, and in
more recent tests has remained at 100% effluent. ITT Rayonier
in—plant toxicity consistantly showed LC5O values below 40%
effluent concentrations prior to secondary treatment (sometimes
as low as 5%). Tests made since secondary treatment show LC5O
503

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levels at 100% effluent concentration, indicating a significant
reduction in toxicity. It should be noted that both mills have
deviated from Washington Department of Ecology (DOE) required
methods during various tests, particularly in earlier tests.
These deviations can result in an implied lower level of toxi-
city due to aeration of test solutions, pH adjustment or other
factors.
A review of the literature on major components of pulpmill
effluents indicates lethal and sublethal toxicities of resin
acids, diterpene alcohols, unsaturated fatty acids and juvabiones.
Although secondary treatment was found to reduce or eliminate the
toxicity of many of these chemicals, a few do not degrade or re-
main toxic. Other toxic components of effluent from both mills
include slimicides, defoamers, dyes and trace metals, although
comparisons of these compounds with pertinent literature is
often not possible. In addition, ITT Rayonier utilizes sub-
stantial amounts of bleach which is known, from the literature,
to be quite toxic alone or to increase the toxicity of other
chemicals in the effluent.
Receiving water bioassays have been conducted annually by WDF
since the 1960’s. During the early 1970’s a large expanse of
area near Port Angeles was highly toxic. The installation of
primary treatment by both mills and ITT Rayonier’s sulfite re-
covery process resulted in significant improvements, although
areas of toxicity were still detectable into the late 1970’s.
The small size of the detected areas may be due to the large
mesh size of the sampling grid coupled with the infrequent nature
of the monitoring.
Studies conducted by Cuminins et al. (1979) prior to secondary
treatment installation by ITT Rayonier showed that oyster larvae
abnormality correlated with SSL levels and that ITT Rayonier
effluents were a major source of toxic response. Little improve-
ment was noted from 1976 data taken by Cardwell et al. (1977);
however many of the samples showed 20% response or less.
504

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Lack of toxic response from receiving water bioassays in some
areas does not necessarily indicate a complete lack of biologi-
cal effect. It is possible that the absence of acute effects
on Pacific oyster larvae is indicative of neither the absence
of chronic, life cycle effects , nor of protection of all impor-
tant biota. A more definitive judgement would rest upon con-
ducting life cycle or 30 to 60 day embryo - juvenile tests and
typing these to effluent concentrations in situ . Testing also
should be expanded to marine organisms and particularly org-
anisms on lower trophic levels. Such test development for
chronic low level environmental contaminants will require a
considerable and extended re8earch effort.
Most aquatic organisms in the study area are potentially affect-
ed by pulp effluents, although documentation is scarce. The
phytoplankton and other marine plants form the productive base
for all other biological organisms. This productivity has been
shown to have been lower for phytoplankton (via chlorophyll
measurements) in the vicinity of the ITT Rayonier outfall prior
to secondary treatment. The literature supports such effects
for plankton; however, no data is available for other marine
plants such as algae or eelgrass. Although the phytoplankton
are a diverse group, the bulk of productivity lies with a few
controlling species, thus presenting a sensitive target to any da-
maging compounds.
Zooplankton are similarly dominated by a few species which form
vital food linkages to the higher food chain organisms. In addi-
tion to providing a food resource, zooplankton include larval
fish stages which are critical to commercial and recreational
fisheries in the area. All of these organisms are subject to
exposure to effluents from the two mills, although potential
effects are not known due to a lack of research.
Shellfish and certain benthic invertebrates are probably the most
sensitive organisms to mill effluents, both physiologically and
5 G5

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in terms of exposure. As filter feeders, shellfish are
physically exposed to higher volumes of contaminants due to
the large volumes of water that they strain in order to find
food. Shellfish are also potential bioaccumulators of many
toxic substances. Since shellfish and many benthos are gen-
erally non—motile in their adult stage, they lack ability to
reduce exposure to toxic compounds through avoidance of pol-
luted waters. It has been shown that there are commercially
and recreationally important shellfish beds in the path of
effluents from both mills, particularly near Ediz Hook, the
shoreline east of Port Angeles, and Dungeness Spit. Previous
studies have shown that shellfish and benthic organisms are
adversely affected by volatile compounds in effluent solids.
Water quality testing recently conducted by EPA (see Shea 1979
and Cummins 1980) indicated that solids from ITT Rayonier ef-
fluent may be precipitating out on bottom sediments or become
entrained in bottom currents in the vicinity of the deep water
diffuser. If confirmed by further studies, this would indicate
previously unsuspected potential effects on benthic organisms.
Both anadromous and marine fish occur in the study area, part-
icularly in the nearshore zones. Salmon and anadromous trout
occur in nearly- all of the streams and rivers and juveniles of
these species inhabit nearshore areas in the track of effluent
from both mills. The Dungeness National Wildlife Refuge provides
particularly attractive habitat for these fish. The areas east
of Port Angeles and near Ediz Hook also provide critical habitat
for spawning Pacific halibut and surf smelt, as well as habitat.
for many other marine species. Many commercially and recreation-
ally important fish species thus occur in habitats exposed to
pulpmil]. effluents.
Wildlife can be expected to be potentially affected by mill ef-
fluent through feeding rather than direct physiological damage.
Important populations of waterfowl and Harbor seals occur both
at Dungeness National Wildlife Refuge and, to a lesser extent,
at Green Point.
506

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Ecological analysis of food flows coupled with existing
limited research on pulpmil]. effects on biota demonstrate
that many marine organisms are potentially affected by effluent
from both mills. In particular many critical species form-
ing food links with primary producers and oraanisms of nearly
all trophic levels are potentially affected. This coupled with
lowered primary productivity of plankton may be seriously
damaging the ecosystem in a chronic, long term manner. Ad-
verse effects on ecological diversity, stability and resili-
ence cannot be demonstrated with the present data base but are
supported by the literature and by the few pertinent studies
conducted at Port Angeles. Such damage at either organism or
ecosystem levels can be expected to have been decreased by se-
condary effluent treatment at Crown Zellerbach and ITT Rayonier
due to documented decreases in toxic contaminants and possibly
improved control over spills and other overflow problems. All
existing physical, chemical and biological evidence indicates
that secondary treatment of pulpmill effluent can, on an over-
all basis, reduce environmental damages to adjacent receiving
waters.
567

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Appendix I-A
GROUNDWOOD PULPING PROCESS

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Appendix I-A GROUNDWOOD PULPING PROCESS
The groundwood pulping process is divided into two major
categories: 1) stone groundwood and 2) refiner groundwood.
Thermomechanical pulping is a modification of the refiner
groundwood process (Edward C. Jordon Co. Inc. 1979). Stone
groundwood pulp is produced by pressing a log transversely
against the outside face of a rotating pulpstone which is
showered with hot water (Gavelin 1966). The pulpstone
surface has evolved from a composition similar to sandstone
to the current abrasive substances such as silicon carbide,
aluminum oxide, modified aluminum oxide and a variety of all
three (Britt 1970). As the grit of the pulpstone surface
passes underneath the wood, compression and expansion of the
wood surface occur to release the wood fibers (Gavelin 1966,
Britt 1970). During this process heat is also generated to
soften the ].ignins and resins binding the wood (Britt 1970).
As the wood is compressed and released fluid is flushed through
the wood mass. This aids in dissolving the binding agents
and releasing the wood fibers (Britt 1970).
As the wood fibers are loosened a mixture of the showering
waters and fibers fall into a grinder pit below the stone
(Gavelin 1966). This stock then overflows to a coarse screen
(Gavelin 1966). After further screening, cleaning, and
thickening on deckers or filters the pulp is diverted to
paper machines (Gavelin 1966).
Refiner mechanical pulping utilizes chips in place of
logs for pulp production. The chips are usually washed in a
chip washer to remove sand, gravel or metal. The chips may
then be diverted directly to the refiner or a screw press for
further chip disintegration (Gavelin 1966). The screw press
fractures the chips into long slender fragments (Gavelin 1966).
A-2

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The reduced chips may then be impregnated with hot water
or a mild chemical solution (Britt 1970). This action
reduces the pitch and removes color bodies from the pulp,
therefore increasing the pulp brightness (Britt 1970). The
chips are then sent to the refiner.
There are three types of refiners presently in use: a
single rotating disc, vertical—shaft single disc, and
double rotating disc (Britt 1970). A cast alloy plate is
attached to each disc which forms the refining surface to
pulp the chips (Gavelin 1966). Depending on the mill,
the facilities usually consist of two to three stages of
refining (Gavelin 1966).
The refiner groundwood pulping process usually consists of
three cleaning stages (one screening and two centrifugal
cleanings) to remove screen rejects (Gavelin 1966). These
rejects can be returned to the first or second stage refiners
or a separate refiner only for rejects (Gavelin 1966). After
thickening the pulp is diverted to paper machines.
Thermochemical pulping differs from refiner groundwood in
that the chips are first softened with heat. During the
refining stages pressure is employed (Edward C. Jordon Co.
Inc. 1979). For more detailed information on these three
types of pulping refer to Gavelin 1966, Britt 1970 and
Charters 1975.
A-3

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Appendix I-B
CROWN ZELLERBACH PROCESSES

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Appendix I-B
RMP, TMP AND REJECT SYSTEMS UTILIZED BY
CROWN ZELLERBACH, PORT ANGELES, WASHINGTON
(Refer to Figure I—B—i)
Source: Hanson 1978
Chips are barged and trucked to the Crown Zellerbach mill
and stored on asphalt. The chips are then screened on a
Radar Disc Screen to remove chips over 3/8 inch thick and
over 3 inches in length. Rejected chips are rechipped.
The chips are washed in a Sprout-Waidron chip conditioner using
mill effluent. Chips are then diverted to a bin which empties
to a recirculating conveyor system that supplies three meter-
ing screws which feed surge bins on each refiner. A flow dia—
grain of the 3 groundwood systems employed by Crown Zellerbach
is shown in Figure I-B-i.
In the TMP (No. 3 line) steaming tube a pressure of 20 to 22
lbs is maintained for 1.5 minutes. Generally newsprint grades
are produced on the TMP line because of the pu].ps superior
strength. Usually the directory grades are produced on the
RMP line utilizing the pu].ps high opacity.
Due to the different requirements for directory and newsprint
puips, different screening options are used. From the third
stage refiners pulp from No. 2 and No. 3 lines is passed over
vibrating knotters. The pulp is then screened on Mark A Cowan
screens with 23% open area. The RMP utilizes smaller screen
sizes (0.065 inch to 0.075 inch newsprint, 0.055 inch to 0.065
inch directory) than TMP (0.085 inch to 0.095 inch newsprint,
0.065 inch to 0.075 inch directory) because TNP fibers are
longer.
On the Reject Refining System pulp passes over a vibrating
knotter to a 0.085 inch Mark A Cowan Screen. The pulp is
then passed over a Bauer cleaner system with recleaners. The
A-5

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RMP SYSTEM
Surge
4tere re /ec
Screen option
23% open area
F ” 1 1 H 0 . 075
Figure I-B-i.
FLOW DIAGRAM OF THE THREE GROUNDWOOD SYSTEMS EMPLOYED BY
CROWN ZELLERBACH, PORT ANGELES, WASHINGTON
1. R.ject optione era eecondary
screening or reject taSte
Source: Hanson 1978

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newsprint pulp requires no further screening but directory
grades are screened over 0.057 inch Cowan screen.
Bleaching also varies for the two grades of pulp. Sodium
sulfite is added to the second stage refiners of the No. 2
and No. 3 pulping lines. Newsprint grades require no fur-
ther bleaching; however, sodium hydrosulfite is added to
directory grades.
A-7

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Appendix I-C
CROWN ZELLERBACH SLUDGEBEDS

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Appendix I-C
SLUDGE BEDS, CROWN ZELLERBACH, PORT ANGELES, WASHINGTON
Throughout its early history until the mid—1960’s, Crown
Zellerbach Corporation discharged fiber bearing wastes into
the Harbor through nearshore discharge pipes. These wastes
formed thick sludge beds which contained anaerobic and poten-
tially toxic materials (USD1 1967). Sludge deposits located
in the western end of the Harbor within the immediate
vicinity of the Crown Zellerbach mill site were dredged in 1953
and 1961 (Aspitarte and Smale 1972). The early dredgings of
1953 removed wastes from the dock face and log pump. In 1961
a total of 60,000 cubic yards (45,600 cubic meters) of sludge
material was removed from the dock front and near the fuel oil
line.
As a result of the Federal — State Conference on the Pollution
of Puget Sound and the Strait of Juan de Fuca (January 16 - 17,
1962) the Federal Pollution Control Commission in 1964 performed
a joint study of sludge beds in Bellingham, Anacortes, Everett
and Port Angeles. Potential detrimental effects were studied
through mapping sludge occurrence and depths as well as through
research on the occurrence of benthic organisms. Extensive
sludge bed deposits occurred in the northwest region of Port
Angeles Harbor, corresponding to the Crown Zel].erbach outfall
and log storage locations, as well as those of the nearby Fibre-
board mill.
In order to comply with permit regulations, Crown Zellerbach
performed a sludge bed survey during 1972. This survey, con-
sisting of three sludge bed studies, concluded that the beds
were in stable condition. After reviewing the study, DOE dis-
continued the requirement for sludge bed removal in the current
NPDES Permit No. WA 000292—5 (Bollen, letter of April 1,
1974). On March 10, 1975 Crown Zellerbach filed an application
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for a proposed dredging site (Thorsen, Public Notice of
March 10, 1975); however, a permit was never issued (Rock,
personal communication of May 7, 1979). As a result dredg-
ing activities have not occurred at the mill site since
1961.
A field toxicity salmon study conducted in 1975 involved a
SCUBA inspection of the mill’s sludge beds (Moore 1976).
The researchers concluded there was no change in sludge bed
appearance since 1961 when Brown and Caidwell (Moore 1976)
performed a SCUBA inspection of the beds, indicating the
beds have stabilized, although anaerobic or toxic compounds
may still exist in these locations.
A-l0

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Appendix I-D
CROWN ZELLERBACH PRI14ARY TREATNENT

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Appendix I-D
PRIMARY TREATMENT, CROWN ZELLERBACH, PORT ANGELES, WASHINGTON
The Dorr-Oliver primary clarifier system used at Crown Zeller—
bach after 1971 requires two pumps operating on a continuous
basis and an additional pump on stand—by. Effluent from the
mill is collected in the clarifier producing floating and
settled solids. Floating solids are skimmed from the surface
and combined with the settled sludge for dewatering. The
settled sludge is pumped through a coil filter (Knudson, letter
of December 9, 1971). Once filtered, the sludge is thickened
in a Reitz-V press, sent to an oil fired hot air dryer for
further dewatering and burned as hog fuel in the steam plant
(Knudson, letter of December 9, 1971 and Chen, letter of Sept-
ember 23, 1977).
Use of the Dorr-Oliver primary clarifier did reduce solids
discharged from the Crown Zellerbach mill, but there is no
available mill data on file at DOE, Lacey, Washington or EPA,
Region x, Seattle, Washington to demonstrate this decrease
(Knudson, letter of December 15, 1971). The early discharge
monitoring reports (DMR) submitted by Crown ZelJ .erbach to DOE
on a monthly basis indicate a TS and suspended combustible
solids (SCS) average for the entire mill effluent discharge;
however subsequent to November 1971 only the characteristics
of the primary treatment plant effluent (014) are represented
in the filed DMP’s. As a result a comparison of effluent mill
solids discharged before and after the installation of primary
treatment cannot be made with the available data.
A-12

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Appendix I-E
CROWN ZELLERBACH SECONDARY TREATMENT

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Appendix I-E
SECONDARY TREATMENT, CROWN ZELLERBACH, PORT ANGELES, WASHINGTON
(Refer to Figure I-E-l)
Previous to the start—up of secondary facilities the mill.
was required by DOE to reduce the effluent flow to be treated
to 12.0 million gallons/day (mgd) to 6.5 mgd (Burkhalter,
letter of September 20, 1977). The mill accomplished this by
closing the stone groundwood mill, zinc hydrosulfite bleach
plant, and the old sawmill. The mill also planned to reclaim
and reuse cooling water and reuse paper machine white water
(Kott, letter of June 28, 1977).
The primary effluent enters the aeration tank containing
bacteria for a specified time period. This allows the bacteria
to consume organic material while utilizing the air provided,
therefore increasing bacterial growth and decreasing organic
material and/or changing its composition. The aerated effluent
is then directed to the secondary clarifier to allow settling
out of bacterial sludge during a 4.5 hour retention time (Rock,
letter of September, 19, 1977). In order to maintain a con-
stant depth of sludge in the secondary clarifier, some of the
sludge is recycled back to the aeration tank (Fenske, personal
communication of October 6, 1980). This also allows for a high
bacterial population in the aeration tanks. The secondary
effluent is discharged from the clarifier through 001.
A-14

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MILL WASTE PRIMARY
CLARIFIER
COIL 1 NUTRIENT AND pH
FILTER CONTROL
________ AMMONIA STORAGE
___ _____ POLYMER PHOSHORIC ACID
PRESS ANDJ TANK GE
SLUDGE I ________ _____________
SLUDGE BURNED -
AS HOG FUEL TANK
SLUDGE
SECONDARY - OUTFALL 001
CLARIFIER
Figure I-E-1. SECONDARY TREATMENT, CROWN ZELLERBACH,
PORT ANGELES, WASHINGTON
Source: Crown Zellerbach Central
Engineering 1977
A-15

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Appendix I-F
CROWN ZELLERBACH OVERFLOWS AND SPILLS

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APPENDIX I-F
The overflows and spills in this section were derived from
available Crown Zellerbach correspondence. There were no
available designated reports on overflows or spills on file
with DOE, Lacey, Washington or EPA, Region X, Seattle, Wash-
ington to indicate such violations; therefore Table I-F-i may
represent a minimum of overflows and spills reported by the
mill.
DMR’s were used to compose maximum violations (greatest allow—
ablevalue for any calendar day) or required effluent para-
meters. The DMR’s (1975 — May 1980) do not indicate specific
daily values of an effluent characteristic but do indicate
the incidents per month in which the required limit of a para-
meter is violated. The exception to this is BOD in which the
mill did not record its violations of the maximum 3,000 lbs/
day limit during July 1977 - September 1978. The DMR’s also
provided the daily average value of a parameter monitored during
the respective month. With the exception of 1977, average and
maximum violations were determined from available DMR’s and
correspondence. Primary Treatment Plant Effluent (PTPE) reports
were available from January - November 1977. These reports
provide the individual daily monitoring for pH, flow, SCS, TS,
zinc and BOD.
A-17

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Table I—F-l. OVERFLOWS/SPILLS RECORDED BY CROWN ZELLERBACH, PORT ANGELES, WASHINGTON
DURING 1971 TO MAY 1980
Violation
120,000 gals, process water,
600 lbs SCS to Inner Harbor
8,150 gals. process water,
85 lbs SCS to Inner Harbor
Lube oil discharge to Inner
Harbor
< 55 gals, diesel oil to
Inner Harbor
Bunker C oil
400,000 gals. process water,
1,700 obs SCS to Inner Harbor
2,200 gals. freshwater
< 1 gal. Bunker C oil to
Inner Harbor
42,000 gals. process water
100 lbs solids to Inner lagoon
5 gals. Bunker fuel oil
Source of
Violation
Power failure
Power failure
Sawmill - hot
condensate outfall
(018)
Oil drum
Flooded sewer
Pump failure
Pump malfunction
Steam plant
1
1
Date
July 24, 1973
August 2, 1973
August 27, 1973
Incidents per
Month
I
N/A
December
February
March 10,
6, 1973
18, 1974
1975
1
1
1
April 24, 1975
July 2, 1975
February 10, 1976
Reference
Orsborn, letter of
July 27, 1973
Orsborn, letter of
August 8, 1973
Springer, letter of
August 31, 1973
Knudson, letter of
December 10, 1973
Kendall, letter of
March 8, 1974
Kendall, letter of March 13,
1975; Knudson, letter of
April 17, 1975
Kendall, letter of
May 5, 1975
Campbell, letter of
July 7, 1975
Kendall, letter of
March 8, 1976
Campbell, letter of
August 19, 1977
June 24, 1977
System malfunction
Abandoned wood
drain line
N/A - No data available on the duration of the violation

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Table I-F-2. TOTAL MONTHS CROWN ZELLERBACH EXCEEDED THE DAILY
AVERAGE BOD 5 PERMIT REQUIREMENT (SUBMERGED OUTFALL
001) DURING JANUARY 1, 1975 - MAY 31, 1980
Permit Requirement 7,000 lbs/day
Month/Year Quantity Reference
(1977)
July 14,900 DMR
August 18,500 DMR
September 14,900 DMR
October 16,700 DMR
November 15,500 DMR
December 17,400 DMR
(1978)
January 15,500 DMR
February 12,000 DMR
March 15,400 DMR
April 15,400 DMR
May 9,700 DMR
June 13,100 DMR
July 14,700 DMR
August 14,800 DMR
(1979)
December 7,840 DMR
(1980)
May 8,640 DMR

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Table I-F-3. TOTAL DAYS PER MONTH CROWN ZELLERBACH EXCEEDED
THE DAILY MAXIMUM BOD PERMIT REQUIREMENT (SUB-
MERGED OUTFALL 001) DdRING JANUARY 1, 1975 -
MAY 1980
Permit Requirement
13,000
lbs/day
Incidents
Month/Year Dates per Month
Reference
(1977)
July 1,2,6—11, 24 DMR, PTPE
15—17 ,19—31
August 1—3,5-31 30 DMR, PTPE
September 1—4,8—30 27 DMR, PTPE
October 1—12,16—29,31 27 DMR, PTPE
November l—9 l1—2l, 26 DMR, PTPE
24—29
December N/A N/C DMR
(1978)
January N/A N/C DMR
February N/A N/C DMR
March N/A N/C DMR
April N/A N/C DMR
June N/A N/C DMR
July N/A N/C DMR
August N/A N/C DMR
(1979)
December N/A 4 DMR
(1980)
March N/A 1 DMR
May N/A 3 DMR
N/A - Not available in information on file at DOE, Lacey, Washington
or EPA, Region X, Seattle, Washington
N/C - The DMR indicates the highest maximum value for the month but
does not indicate total incidents; therefore at least one
incident/month is verified
A-20

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Table I-F-4. MONTHS CROWN ZELLERBACH EXCEEDED THE DAILY MAXIMUM
SCS PERMIT REQUIREMENT (SUBMERGED OUTFALL 001)
DURING JANUARY 1, 1975 - JUNE 30, 197 7*
Month/Year
Dates
Permit Requirement
8,000 lbs/day
Incidents
Per
Month
Reference
1975
4
1
DMR; Nadig,
September
letter of
Sept. 8, 1975
*Subsequent to July 1, 1.977 the mill was required to monitor TSS.
Table I-F-5. TOTAL MONTHS CROWN ZELLERBACH EXCEEDED THE DAILY
AVERAGE TSS PERMIT REQUIREMENT (SUBMERGED OUTFALL
001) DURING JULY 1., 1977 — May 31, 1980
Month/Year
Permit
Requirement
10,000
lbs/day
Quantity
Reference
(1977)
November
12,978
DMR
(1978)
January
February
14,090
10,370
DMR
DMR
(1979)
December
13,190
DMR
(1980)
May
13,520
DMR
A-21

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Table I-F-6. TOTAL DAYS PER MONTH CROWN ZELLERBACH EXCEEDED
THE DAILY MAXIMUM TSS PERMIT REQUIREMENT (SUB-
MERGED OUTFALL 001) DURING JULY 1, 1977 -
MAY 3]., 1980
Month/Year
Dates
Permit Requirement
19,000
lbs/day
Incidents per
Month
Reference
(1977)
November
3-5
3
DMR
December
N/A
2
DMR
(1978)
January
N/A
9
DMR
July
N/A
2
DMR
(1979)
March
14,29
2
DMR
July
5,13
2
DMR
August
17
1
DMR
December
N/A
8
DMR
(1980)
January
6
1
DMR
February
5,20
2
DMR
March
N/A
2
DMR
April
11,12,13,15
4
DMR
May
N/A
6
DMR
N/A — Not available in information on file at DOE, Lacey, Wash-
ington or EPA, Region X, Seattle, Washington
A— 22

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Table I-F-i. TOTAL DAYS PER MONTH CROWN ZELLERBACH EXCEEDED THE
DAILY MINIMUM pH PERMIT REQUIREMENT (SUBMERGED OUT-
FALL 001) DURING JULY 1, 1977 - MAY 31, 1980
Permit Requirement 5.0
Month/Year Dates Incidents Per Month Reference
(1977) 20 1 DMR, PTPE
November 20 1 DMR, PTPE
(1978)
October 29 ,30 2 DMR
(1979)
May N/A 4 DMR
June N/A 1 DMR
(1980)
February 4 1 DMR
May N/A 4 DMR
N/A - Not available in information on file at DOE, Lacey, Wash-
ington or EPA, Region X, Seattle, Washington
Table I-F-8. TOTAL DAYS PER MONTH CROWN ZELLERBACH EXCEEDED THE
DAILY MAXIMUM pH PERMIT REQUIREMENT (SUBMERGED OUT-
FALL 001) DURING JULY 1, 1977 - MAY 31, 1980
Permit Requirement 9.0
Month/Year Dates Incidents Per Month Reference
(1978)
July 12,13 2 DMR
A-23

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APPENDIX I—G
THE SULFITE PROCESS

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Appendix I-G THE SULFITE PROCESS
The following excerpt on the sulfite process is extracted
airectly from Vogt and Kinch 1976:
The sulfite process is used to make two distinct-
ly different types of pulp -— papermaking grades
and dissolving grades. The basic process is
the same for both, although there are signifi-
cant differences in cooking temperatures, strength
of chemical application, and bleaching practices.
The following discussion of sulfite pulping is
generally applicable to both. The major differ-
ences in its application to dissolving pulp are
noted at the end of this discussion, and the
variations in bleaching are covered under “Bleach-
ing of Chemical Pulp.”
In the sulfite process, wood chips are cooked
with acidic solutions of the sulfites of calcium,
magnesium, ammonia, or sodium. The cooking
liquor is manufactured at the mill from pur-
chased and recovered chemicals.
Sulfurous acid is prepared by absorbing sulfur
dioxide in water. Sulfur dioxide is made at the
mill by burning sulfur or is purchased in liquid
form either of which is supplemented by that
returned to process from the sulfur dioxide
recovery system.
In ammonia base mills, aqua ammonia is reacted
with sulfurous acid. If the chemical is pur-
chased in the anhydrous form, it is first put
into solution. Ammonia is not recovered.
When cooking is completed, the pulp is blown
into a blow tank. It is then delivered to
multi—stage vacuum washers on which counter-
current washing separates the spent liquor
form the pulp. In some cases, blow pits rather
than tanks are employed where the pulp is washed
by diffusion of wash water through the pulp mass.
It is possible to recover 95 percent of the
liquor solids by vacuum washing, but the limit
is about 85 percent from displacement washing
in blow pits. A 15 percent liquor concentra-
tion is obtainable by vacuum washing while the
highest solids concentration attainable by
blow-pit washing is about 10 percent. Of f-
gases are passed to an absorption system for
recovery of their sulfur dioxide content. After
washing,, the pulp is diluted, screened, centri-
fugally cleaned, and deckered to the desired
stock chest consistency for bleaching.
A-25

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The weak red liquor separated from the pulp is
evaporated to a consistency of 50 to 60 percent
solids which is suitable for burning. Forced
feed evaporators must be used for ammonia base
liquor because of its high viscosity. Ammonia
base liquor is burned either in a typical re-
covery furnace or a fluidized bed unit and
sulfur dioxide is stripped from the off—gases
for use in the liquor preparation unit.
In the preparation of sulfite dissolving puips,
the wood is cooked at a higher temperature than
for papergrade pulps. Cooking is continued
until most of the lignin and part of the cellu-
lose are dissolved whereas in papermaking puips
only the lignin is dissolved. The resulting
spent liquor thus has a higher solids content
when burned. In addition to screening to re-
move bark and wood particles after the pulp is
washed, it is often sent through special “side—
hills” screens for thickening and to separate
resinous materials.
Dissolving pulps are always bleached, and, in
addition, usually must undergo one or more
additional reactions such as chemical purifica-
tion, deresination, ash removal, etc. Most
of these steps are combined in a complex bleach-
ing and purification process.
The purpose of the caustic extraction stage in
bleaching dissolving sulfite puips is somewhat
different from its function in bleaching sul-
fite paper grade puips. In the latter, this
stage is used to remove partially bleached
material solubi].ized in the chlorination stage.
In the manufacture of dissolving pulp, the ex-
traction stage is much more drastic in terms
of caustic concentration and degree of heat
in order to dissolve a specific fraction of the
cellulose itself which is not suited to the
manufacture of rayon. Over 45 kg (100 lb) of
caustic may be added per kkg (ton) of pulp and
reaction temperatures exceed the boiling point
while only about 14 kg (30 ib) of caustic
under warm conditions are required for paper
grade pulp (180). In dissolving pulp bleaching,
this step dissolves from 15 to 30 percent of
the pulp, depending on the grade of cellulose
desired.
A-26

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Appendix I-H
DISSOLVING PULPS

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Appendix I-H TYPES OF DISSOLVING PULPS
The following excerpt on the types of dissolving puips is
extracted directly from Vogt and Kinch 1976:
Dissolving pulps are highly purified forms of
cellulose which are used in the manufacture of
rayon, cellophace, methyl cellulose, ethyl
cellulose, nitracellulose, cellulose acetate,
and other cellulose derivatives. Dissolving
sulfite differs from paper grade sulfite pulp
in that it contains a higher percentage of
alpha cellulose and a lower percentage of hemi—
celluloses. The extra degree of purity is
obtained primarily by hot caustic extraction
during the bleaching operations. Also the
cooking conditions are sometimes somewhat more
severe than for papergrade pulp (i.e., a high-
er cooking temperature and a shorter cooking
time). The unbleached yields for dissolving
puips are about the same as for papergrade sul-
fite pulp. Most of the additional purification
required by the dissolving pulps comes in
the bleaching, more specifically in the hot
caustic extraction stage. For this reason the
shrinkage in the hot caustic extraction is
the most important factor in identification of
the different grades of dissolving puips.
There are four basic grades of dissolving wood
pulp which are commonly produced by the sulfite
process. These are: (1) nitration grade, (2)
viscose grade, (3) cellophane grade and (4)
acetate grade. The properties, mainly the alpha
cellulose content and the viscosity of each of
these grades is varied to provide the properties
which are desirable for its particular end use.
Nitration grade dissolving sulfite pulp has
a hot caustic extraction shrinkage of 8 — 12% and
an alpha cellulose content of 92% or higher. For
most end uses the purity of nitration grade
pulp is not as critical as for acetate grade
pu].ps. One exception to this is for explosive
grade pulp which requires an extremely pure
pulp with an alpha cellulose content of 98%.
Nitration grade puips find their end uses en-
tirely in non—fiber purposes, which are used
primarily in the manufacture of plastics and
lacquers.
A-28

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Viscose grade dissolving sulfite pulp has
a hot caustic extraction shrinkage of 13—17%
and is used in the manufacture of rayon, which
is the largest use of dissolving pulp. Pulp
to be used for rayon manufacture generally has
an alpha cellulose content in the range of
88 to 91%.
Cellophane grade dissolving pulp has a hot
caustic extraction shrinkage of 17—23% and an
alpha cellulose content of 89% and higher.
The most important property of this pulp is
its solution viscosity, because it determines
the viscosity of the casting solution. The
difference between the cellophane and vis-
cose grades is that cellophane grade pulp
undergoes a slightly higher degree of hot
caustic extraction.
Acetate grade dissolving sulfite pulp has a hot
caustic extraction shrinkage of 24% or higher.
Acetate puips normally have an alpha cellulose
content of 95.0—96.5. Acetate grade pulp is
used for both textile fiber purposes and for
non fiber purposes. The fiber uses include
regular tenacity yarn and acetate filament
yarn. The requirements of pulp used in the
manufacture of cellulose acetate are much
stricter than those for rayon grades. This
pulp must be relatively free of pentosans, de-
graded cellulose and other non—cellulosic
materials. These materials in the pulp
produce a hazy solution, lower the yield, re-
duce the recovery of chemicals and impare the
physical and chemical properties of the cellu-
lose derivitives.
A-29

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Appendix I -I
ITT RAYONIER PRIMARY TREATMENT

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Appendix I—I
PRIMARY TREATMENT, ITT RAYONIER, PORT ANGELES, WASHINGTON
In order to direct all their process waste discharge through
outfall 007, the mill constructed several sunip pumps to direct
mill waste to the clarifier or directly to the outfall. Mill
effluent entering the clarifier is retained for a specified
time period to allow settling of solids. A rotating skimmer
removes the floating solids. Presently both the floating and
settleable solids are dewatered by use of a Komlin-Sanderson
filter and Rietz—”V” press and incinerated or mixed with se-
condary sludge to increase its consistency, dewatered in a
Tait-Andritz press and landfilled (Button, letter of January
19, 1978; Owens, letter of November 12, 1979 and Fenske,
personal communication of August 26, 1980).
Primary treatment facilities were installed for the purpose
of reducing solid components in the mill effluent. Removal
of these solids lowers the organic components in the waste
and hence its oxygen demand. The mill’s average daily dis-
charge of SCS was reduced by approximately 65% after primary
treatment became operative (Table I—I-i). The mill’s monitored
and recorded concentrations of its daily total solids (TS)
discharge indicate little or no change subsequent to primary
treatment. Considering pulp production remained constant
and the SCS discharge decreased with primary treatment, there
is no evident explanation in the available information to
indicate why the TS level did not also decrease after clari-
fication.
A-31

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Table I-I-i. MONTHLY AVERAGES OF SUSPENDED COMBUSTIBLE SOLIDS AND
TOTAL SOLIDS AT ITT RAYONIER, INC., BEFORE AND AFTER
INSTALLATION OF PRIMARY TREATMENT (THOUSAND LBS/DAY)
Suspended
Combustible Total
Month Year Solids Solids
January 1972 37.7 1,555
February 38.7 1,693
March 49.7 1,548
April 47.7 1,245
May 50.3 1,592
June 44.9 1,469
July 36.4 1,411
August 55.7 1,365
September* 8.5 1,635
October 10.9 1,493
November 13.6 1,385
December 13.5 1,241
January 1973 11.7 1,516
February 10.9 1,395
March 13.0 1,484
April 11.6 1,470
May 13.3 1,355
June 13.0 1,331
* Primary Treatment operational
A-32

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Appendix 1-3
ITT RAYONIER SLUDGE BEDS

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Appendix i-j
SLUDGE BEDS, ITT RAYONIER, PORT ANGELES, WASHINGTON
As a result of the 1962 Puget Sound Enforcement Conference,
a joint Federal—State investigation of bottom deposits in the
Harbor were initiated in 1964. Deposit measurements and
biological analysis of the Harbor showed large sludge build-
ups on the east and west sides of the ITT Rayonier mill, as
well as an area north of the mill at outfall 003. In the
early 1970’s as required by their 1970 permit (No. T—2867)
from the Water Pollution Control Commission, Stipulation
No. 9586, ITT Rayonier began applications for dredging per-
mits to remove sludge from these areas. However, in Sept—
ember 1973, agreement was reached between the mill and the
state and federal governments that the sludge beds would be
allowed to recede naturally through water action, and that
dredging would not be necessary (Knudson, letter of September
14, 1973).
Permits for dredging the log storage yard areas were granted
by the U.S. Army Corps of Engineers in August 1974 for
a three year period. Dredging did occur in October 1974
(ITT Rayonier, Monthly Environmental Report (MER), October
1974). Other dredging may have occurred during the ensuing
three year period (1974—1977) but is not referenced in the
monthly environmental reports published by the mill.
In 1977 ITT Rayonier requested DOE’S position on their fil3.—
ing of 1ogpo ds as an alternative to water storing their logs
(Rock, letter of February 18, 1977; Rock, letter of March 28,
1977). An application made to the Corps of Engineers in Jan-
uary 1978 for a 3 year permit to dredge material from the log
storage area west of the mill indicates the log area was never
filled; however there is no further available correspondence
to indicate if a 3 year dredging permit was granted (Baxter,
Public Notice of January 27, 1978).
On June 13, 1977 DOE approved dredging on the west side of the
mill in the chip unloading area only (Rock, letter of June 13, 1977).
A-34

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Appendix I-K
ITT RAYONIER SECONDARY TREATMENT

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Appendix I-K
SECONDARY TREATMENT, ITT RAYONIER, PORT ANGELES, WASHINGTON
(REFER TO FIGURE I—K—i)
Lime and other chemical additives are piped into the acidic
effluent from the primary clarifiers and strong sewer before
entering the deep aeration tanks (DOE 1978). This controls
pH and foam. The effluent then enters one of two 70 foot (21.34
m) high aeration tanks and is retained for approximately 8
hours before diversion to the secondary ciarifiers (DOE 1978).
The biological mass contained in the tanks utilizes oxygen
to assimilate waste organic compounds which lowers the
effluent’s BOD and indirectly increases the concentration
of organisms (DOE 1978). In order to replenish the dissolved
oxygen consumed by the biological mass of bacteria, air is
pumped through the bottom of the tanks (Swingle, letter of
May 2, 1978).
From the aeration tanks the effluent under pressure enters
one of two parallel secondary clarifiers which are at
atmospheric pressure. This reduction in pressure allows
dissolved gases to be released forcing the biological solids
to the surface for removal and the effluent is discharged
to the Straits (DOE 1978). These solids are skimmed from
the surface of the clarifiers and either recycled to the
aeration tanks to maintain a high bacteria population or
mixed with primary sludge, dewatered and buried in the Shot—
well gravel quarry (DOE 1978; DOE 1979 and Owens, letter of
November 12, 1979). The water from the dewatered sludge is
returned to the treatment facilities (DOE 1979). As indicated
in Section I.C.l, in the near future secondary sludge will
be dried by the Carver/Greenfield system and incinerated.
A-36

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* Dswafsr.d
and
Lsndf 11Usd
Waste
Sludge
Deep
Tank
Effluent
Recycled
Sludge
001 Foam
Tank
* Soon to be dried by Carver/Greenfield System and incinerated.
Figure I—K-i. Flow diagram of secondary treatment facilities, ITT Rayonier, Port Angeles,
Washington
Source: ITT Rayonier, N.W. Central Engineering Division 1977

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Appendix I-L
ITT RAYONIER SSL RECOVERY

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Appendix I-L SSL WASTE RECOVERY SYSTEM
ITT RAYONIER, PORT ANGELES, WASHINGTON
The following excerpt was extracted directly from ITT
Rayonier, No Date, located in 1977 DOE files, Lacey, Washington:
Spent sulfite liquor (SSL) originates in the
cooking process where wood chips are converted
to wood pulp. The chips and cooking acid, a
mixture of ammonia, water and sulfur dioxide,
are subjected to high temperature and pressure.
During this process about half of the dry weight
of the wood is solubilized leaving the cellulose
fibers as the solid component -— wood pulp.
The liquid portion, a mixture of the spent cook-
ing acid and the solubilized wood, is SSL.
The ammonia base SSL recovery process with a
number of special energy conservation features
was eventually selected for SSL destruction.
This process includes several major steps:
LIQUOR COLLECTION: SSL is separated from the
pulp on a series of multistage washers. The
system was designed to capture 95% of the SSL
even though the requirement called for only
85%.
SULFUR DIOXIDE REMOVAL: A portion of the sulfur
dioxide is stripped under pressure and returned
to the pulp mill acidmaking process. This
stripping system was included in the process
ahead of SSL evaporation to maximize thermal
efficiency of the following evaporation step.
EVAPORATION: SSL is concentrated from about
10% dissolved solids to about 50% in a combina-
tion vapor recompression and multiple effect
evaporator system. In this system steam tur-
bine driven units rather than electric motors
are used, thus avoiding the purchase of over
500 KW of electrical energy.
INCINERATION: Concentrated SSL is burned in
a large recovery furnace where the released
heat is converted to about 400,000 pounds per
hour of steam.
AIR EMISSION CONTROL: Sulfur dioxide is scrubbed
from the stack gases with an ammonia solution
and is recycled back to the cooking process.
Finally, the stack gas is passed through fiber-
glass filters to remove particulate matter.
A-39

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At ITT Rayonier’s Port Angeles pulp mill a
major waste disposal problem has been solved
with the installation of a $30 million
recovery system. Together with a new $2.3 mil-
lion boiler for burning solid wood wastes,
the recovery boiler has allowed ITT Rayonier to
generate nearly all of the mill’s steam and
one-third of its electrical power needs from
wood wastes. Thus, while solving a water pol-
lution problem, Rayonier has been able to save
400,000 barrels of fuel oil per year.
A-40

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Appendix I-M
ITT RAYONIER SPILLS AND VIOLATIONS

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Appendix I-M VIOLATIONS
Overflows and spills are described in Table I-M—i• The over-
flows usually represent mill discharge from a location other
than the permitted 001 (previously 007). Spills also indi-
cate an unauthorized discharge from an unpermitted point source,
Each counted incident recorded in Table I-M-l is based on a
24-hour period; therefore an incident may indicate an over-
flow for a short period or may represent a continous 24—
hour overflow. Unless continuous, overflows from the same
source that occurred more than once within a 24—hour period
were counted separately whenever the information provided
such data.
The overflow/spill violations were derived from available
Monthly Environmental Reports (MER), Monthly Environmental
Summaries (MES) , Daily Environmental Summaries (DER), Primary
Treatment System Overlow Logs (PTSOL) and correspondence.
The DER’s and PTSOL’s which offered the most complete infor-
mation were only available from December 31, 1977 to April
30, 1980 and March 1, 1979 to June 30, 1980, respectively.
Both maximum and average limits for specific effluent charac-
teristics (BOD, SCS and TSS) were first required in NPDES
permit No. WA 000079-5, issued to ITT Rayonier August 30,
1974. The pH limits initially required on July 1, 1977
(Permit No. WA 000079—5) referred to minimum (5.0) and maximum
(9.0) limits. The minimum and maximum limits refer to the
smallest and greatest allowable value for any calendar day
(Permit No. WA 000079-5). The average limits were determined
from the measured values over a calendar month’s time (Permit
No. WA 000079—5). The 15% SSL solids discharge limit
required by Stipulation No. 9586 and Permit No. WA 000079—5
were determined from a 14—day moving average.
A-42

-------
Violations of these effluent limitations during January 1975
to June 1980, unless indicated differently, were derived
from available Discharge Monitoring Reports (DMR) representing
monthly summaries, ITT Rayonier’s Submerged Outfall Charac-
teristics (SOC) computer print out sheets representing daily
monitoring, the mill’s Raw Waste Load Information (RWLI)
representing daily monitoring and individual correspondence
(Tables I—M—3, I—M—4, I—M-9, I—M—10). These summary Tables
may represent a minimum of violations due to incomplete
available information. The following indicates dates of
availability: DMR(January 1975 — June 1980) and SOC (Janu-
ary 1976 — June 1978, March 1979 — May 1980). Additionally
not all parameters were always recorded in these reports.
The SSL 14-day moving averages CTable I-M-2) were calculated
from available computer print out sheets entitled Summary of
SSL Data (June 1977 — May 1978) and EPA’S moving average
calculations from May 14, 1978 — April 30, 1979 (Bodien,
July 31, 1978 — January 10, 1979). Due to the limited avail-
ability of SSL solids data this report only provides a sum-
mary of those 14-day averages exceeding the required 15% mini-
mum discharge of the mill’s total generated SSL solids at
more than 312,000 lbs/day (141,523 kg/day) from June 1977 to
July 1979.
On August 29, 1979 permit WA 000079—5 expired; however a new
permit was not issued to the mill until September 12, 1980
(Dagelen, personal communication of October 1, 1980). As a
result violations occurring during August 1979 to early Sept-
ember 1980 were determined according to the limits set in the
NPDES permit (No. WA 000079—5) issued August 30, 1974.
A-43

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Table I—M—1.OUTFLOW/SPILLS RECORDED BY ITT RAYONIER, PORT ANGELES, WASHINGTON
Source: See “Reference” Column
Incidents
Month—Date Source of Violation Per Month Reference
(1975)
FEB N,Aa Unauthorized Discharge to Ennis Creek 1 Knudson, letter, 20 Feb 1975
APR N/A Woodmill Pumping Station Intermittent PIER
MAY N/A “ “ “ N/A
JUN N/A “ “ “ N/A
AUG N/A “ “ N/A
SEP N/A “ “ “ N/A
OCT N/A “ “ “ Periodic
NOV N/A “ “ “ Intermittent
N/A Cordwood Deck Sump N/A
DEC N/A Woodmill. Pumping Station Intermittent
N/A Woodyard Drainage Sump Intermittent ‘I
N/A Cordwood Deck Sump Intermittent
(1976)
JAN N/A Woodinill Pumping Station Intermittent
N/A Outfall D Constantly
N/A Cordwood Deck Sump Intermittent
N/A Woodyard Drainage Sump Intermittent
FEB N/A Woodmill Pumping Station Intermittent
N/A Outfall D Constantly ITT Rayonier Quart . Rev., 6 Oct 1976
N/A Woodyard Drainage Sump Intermittent MER
N/A Cordwood Deck Sump Intermittent
N/A Pulp Mill Pumping Station Intermittent
a N/A = Not Available in information on file at DOE, Lacey, Washington or at EPA, Region X.

-------
Table I—M—1.CONTINUED, p. 2.
Incidents
Month—Date Source of Violation Per Month Reference
(1976)
M&R N/A Woodmill Pumping Station to Ourfall A 140 Hrs. MER
N/A Woodyard Drainage Sump to Outfall E Almost MES
Constantly
N/A Clear Sewer to Outfall C 1 Hr.
N/A Outfall D Constantly ITT Rayonier Quart . Rev., 6 Oct 1976
APR N/A Woodmill Pumping Station to Outfall A 159 Hrs. MER and MES
N/A Woodyard Drainage Sump to Outfall E Constantly “ “
N/A Outfall D (freshwater ground drainage) Constantly “ “ “
N/A Outfall C 8 — 10 Hrs. “ “ “
N/A Broke Repulper to Ennis Creek 15 mm. “ ‘ H
M&Y N/A Woodyard Drainage Sump to Outfall E Constantly MES, May, Jun, 1976
N/A Outfall D Constantly “ S U II
10 SSL Lagoon Leak N/A MER
JUN N/A Woodyard Drainage Sump to Outfall E Constantly MES, May, Jun, 1976
N/A Outfall D Constantly “ “ “ “
JUL N/A Woodyard Drainage Sump to Outfall E Constantly MES
N/A Outfall D Constantly
AUG N/A Outfall D Constantly ITT Rayonier Quart . Rev. 6 Oct 1976
SEP N/A Outfall D Constantly U I’
O T N/A Woodyard to Outfall E 22% MES
N/A Outfall D 58% MES
N/A Spills to all Outfalls N/A MES
NOV N/A Clorine Generator Sump 1 180—240 gal.
b

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Table I-M—lCONTINUED, p. 3.
Incidents
Month—Date Source of Violation Per Month Reference
(1977)
JAN N/A Outfall D Constantly Rogers, technical report, 7 Jan 1977
N/A Gas or Diesel Pump to Outfall D N/A Rogers, letter,13 Jan 1977
N/A Ground Drainage by the Woodmill N/A ‘S
N/A Pumping Station to Bay N/A “ “
APR 19—23,
27—29 Woodmill Pumping Station 8 days HER
N/A Woodyard Drainage Sump to Outfall E Almost Daily
N/A Cordwood Deck Sump Occassionally
N/A Outfall D Constantly
MAY N/A Woodyard Drainage Sump N/A
N/A Cordwood Deck Sump Occassionally
N/A Outfall D N/A
1,2,5—8, Pulp Mill Pumping Station (solids
18—20 sewer received no primary clarification) 9
JUN N/A Spills to all outfalls 3
N/A SSL Leak to Shoreline few hours
JUL 29 Chioring Dioxide Leak to Ennis Creekb N/A Cameron (DE 77—423), 31 Aug 1977
N/A Outfall D 48% “
N/A Outfall E 23% “
AUG N/A Outfall E 23 HER
N/A Cordwood Deck Sump 5
N/A Outfall D 20
N/A Effluent from Tank Vent N/A Hawk, letter, 26 Aug 1977
N/A Pond of Effluent North of Primary
Clarified N/A
b
Produced fish kill.

-------
Table I—M—]. CONTINUED, p. 4.
Incidents
Month—Date Source of Violation Per Month Reference
(1977)
SEP N/A Cordwood Deck Sump 5 MER
N/A Outfall C 5 II
N/A Outfall D 17
N/A Outfall E 17
OCT N/A Outfall E N/A Rogers, letter, 18 Oct 1977
NOV N/A Outfall E N/A MER
DEC N/A Outfall E N/A
N/A Cordwood Deck Sump N/A DERC
(1978)
JAN 117 Woodyard Drainage Sump to Outfall E 2 DER
1—5,9—12 Cordwood Deck Sunip 8
9—12,29 Outfall D 5
18,27 Pulp Mill Pumping Station 2
FEB 2,5—7,
13,19,20,
21,28 Pulp Mill Pumping Station to Outfall C 8 It
6,7,9—17 Woodmill Pumping Station to Outfall A 11
6—11 Woodyard Drainage Sump to Outfall E 6
11,12 Outfall D 2
MAR 20,21 Pulp Mill Pumping Station to Outfall C 2
31 Outfall D 1 1
31 Cordwood Deck Swamp 1
APR 1—3,19 Outfall D 4
12,13,17 Pulp Mill Pumping Station to Outfall C 3
19—26,28—30 Woodyard Drainage Sump to Outfall E 11
21 Cordwood Deck Swamp 1
CAvailable DER’s (Dec 1977 to Apr 1980)

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Table I—M—l.CONTINUED, p. 5.
MAY 1,11—13,
(1978) 15—18,21,
26,30
1,3,4,5,8,
9,16,17
1,2
6,18,26
10
19
JUN 4,5,12
9
16,27
JUL 1
5
11,12
13
14
AUG 10
26,28
29
SEP 6,7
OCT 23
NOV 2-6
14
18
DEC 16,17
10
8
2
3
1 (2.5 Hr.)
1
3
1
2
1
1
2
1
1
1
2
1
2
1
5
1
1
‘I
I,
II
I,
II
‘I
I,
‘I
I,
‘I
II
tu
‘U
‘U
‘I
I,
Incident8
Month—Date Source of Violation Per Month Reference
DER
‘I
‘U
‘I
Rogers, telephone, 11 May 1978
DER
Pulp Mill Pumping Station to Outfall C
Woodyard Drainage Sump to Outfall E
Outfall D
Woodmill Pumping Station to Outfall A
Sodium Chlorate spill to Ennis Creek
(through old trench)
Cordwood Deck Sump
Woodyard Drainage Sump to Sout fall E
Cordwood Deck Sump
Woodmill Pumping Station to Outfall A
Spill to Log Storage Pond
Woodmill Pumping Station to Outfall A
Outfall D
Woodyard Drainage Spill
Cordwood Deck Sump
Spill to Emergency Overflow
Woodmill Pumping Station
Pulp Mill Pump Station
Cordwood Deck Sump Pump
Woodyard Drainage Pump
Woodyard Drainage Pump
Pump Station Failure
All Pumps Down, causing spill (power out)
Woodyard Pump Station to Outfall E
2
U’

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Table I—M—3 CONTINUED, p. 6.
Incidents
Month—Date Source of Violation Per Month Reference
(1979)
JAN 5—7 Pulp Mill Pump Station 3 DER
718 Woodmill Pump Station 2
11,13,21 Woodmill Sump 3
JAN 7,3 Cordwood Deck Sump 2
7,9,13 Woodyard Drain Sump 3
15 Clarifier Overflows Causing Foam and
Liquid Seepage Along Shoreline 1
15 Pump down 1 (1/2 Hr.)
17 Clear Sewer Pump 1 1
23 Finishing Room Sump 1 1
FEB 1 Woodyard Drainage Sump Pump 1
1,21,26 Cordwood Deck Sunip Pump 3
1,8 Woodmill Pumping Station 1
8 Woodmill Sump Pump 1
27,28 Outfall D 2
MAR 1—3,5,6,
9,20—23, d
25—27,30 Cordwood Deck Sump 11 PTSOL
2 Pulp Mill Pumping Station to Outfall C 1 PTSOL, DER
8,16,20,24 Woodmill Pumping Station 4 PTSOL
22—28 Emergency Overflow from Finishing Sump
to Outfall D 7 PTSOL, DER
30 Emergency Overflow for Pulp Mill
Pumping Station to Outfall C 1 “
dAilbi PTSOL’s (Mar 1979 to Jun 1980).

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Table I—14—]..CONTINUED, p. 7.
Incidents
Month—Date Source of Violation Per Month Reference
(1979)
APR 2 Cordwood Deck Sump 1 PTSOL
8,9,19 Woodmill Pumping Station 2 PTSOL, DER
9,13,18,
20,24 Pulp Mill Pumping Station 5
7 Outfall D 1 DER
MAY 7,18 Pulp Mill Pumping Station 2 PTSOL
9,14,15,16 Woodyard Drainage Sump 4
JUN 4 Finishing Room Sump 1
11,25,26 Wood Mill Pumping Station 3
25 Pulp Mill Pumping Station 1 1
JUL 9—15 Finishing Room Sump 15 PTSOL, DER
12,26 Cordwood Deck Sump 2 PTSOL
23,28,29—31 Woodyard Drainage Sump 5
27,28,31 Woodmill Pump Station 3 I’
AUG 1—17 Woodyard Drainage Sump 17
1,7,22,23,
25—31 Woodmill Pumping Station 11 I’
3,5 Cordwood Deck Sump 2
7 Finishing Room Sump 1
9 Pulp Mill Pump Station 1 DER
10 Bypass of Primary Clarifier thru 1 Neel, letter, 15 Aug 1979
Outfalls A, C, and D
SEP 2—6 Woodmill Pumping Station 5 PTSOL
17—30 Woodyard Drainage Sump 14 I’
25 Pulp Mill Pumping Station 1

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Table I—M—].CONTINUED, p. 8.
Month—Date
(1979)
Source of Violation
Incidents
Per Month
References
OCT 7,17,24
10,12
1—5
NOV 16
11,13,14,16,
18,19,21,
23,26—28
1,5,6,16
5,6,23,24
16
16
DEC 13,28,29
1—6,20
1—7,10,30,
31
13
(1980)
Woodmill Pumping Station
Pulp Mill Pumping Station
Woodyard Drainage Sump
Pulp Mill Pumping Station
Woodmill Pumping Station
Woodyard Drainage Sump
Finishing Room Sump
Cordwood Deck Sump
Clear and Solids Sewer
Pulp Mill Pumping Station
Woodmill Pumping Station
Woodyard Drainage Sump
Solids Sewer and Clear Sewer
25
4
4
1
1
3
7
7
1
PT SQL,
I,
‘S
DER
PT SQL
‘I
PTSOL, DER
DER
JAN 12
1,2,6—14,
16—2 0
4—9,15,17
12
12
FEB 2,3,4,7,15
6,12
15
19,20
3
Pulp Mill Pumping Station
Woodyard Drainage Sump
Wood Mill Pumping Station
Finishing Room Sump
Cordwood Deck Sump
Woodmill Pumping Station
Woodyard Drainage Sump
Pulp Mill Pumping Station
Finishing Room Sump Pump
Cordwood Deck Sump
1
15
11
1
1
5
2
1
2
1
PTSOL, DER
PT SQL
DER
I,
PTSOL
I,
‘I
SI
DER
3
2
5
1 ‘S
PT SQL
5,
I,
DER
I’
‘5
‘S
PTSOL

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Table I—M—1.CONTINUED, p. 9.
Incidents
Month—Date Source of Violation Per Month Reference
(1980)
MAR 4—6,10,
11,13 Finishing Room Sewer 6 PTSOL, DER
5,29 Woodyard Drainage Sump 2 PTSOL
11 Woodinill Sump 1
19,20 Cordwood Deck Sump 2 PTSOL, DER
28 Clear Sewer 1 It
APR 5,10—14 Woodyard Drainage 6 PTSOL
12 Cordwood Deck Sump 1
14,15,21 Finishing Room Sump 3 DER
15 Pulp Mill Pumping Station 1 DER
MAY 31 Woodyard Drainage Sump 1 PTSOL
JUN 9 Cordwood Deck Sump
23 Lime Flow to Bay, Pipe Carrying Lime
Slurry Ruptured 1 Libby, letter, 23 Jun 1980

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Table I-M-2. TOTAL DAYS ITT RAYONIER EXCEEDED THE 15% SSL SOLIDS
14.-DAY MOVING AVERAGE FROM JUNE 1977 TO JULY 1979
Source: 10 August 1977 to 27 February 1978:
ITT Rayonier, Summary of SSL data computer
print—out sheets
31 July 1978 to 10 January 1979:
Bodien, 1980. EPA Calculations of SSL data.
SSL
TOTAL
PERCENT OF
TOTAL SSL
DATE GENERATED
DISCHARGE
DISCHARGED
(1977)
AUGUST
10 1,285,000 200,000 15.6
11 1,279,786 218,286 17.1
12 1,300,286 248,071 19.1
13 1,295,143 275,643 21.3
14 1,295,429 287,857 22.2
15 1,260,643 303,143 24.0
16 1,340,357 297,643 22.2
17 1,420,357 308,500 21.7
18 1,463,786 311,214 21.3
19 1,475,500 304,500 20.9
20 1,462,071 306,929 21.0
21 1,458,929 315,286 21.6
22 1,452,071 324,643 22.4
23 1,454,429 341,714 23.5
24 1,441,071 339,143 23.5
25 1,448,286 333,929 23.1
26 1,449,500 321,571 22.2
27 1,451,000 327,286 22.6
28 1,447,000 344,714 23.8
29 1,494,714 363,214 24.3
30 1,485,286 389,214 26.3
31 1,483,643 402,786 27.2
SEPTEMBER
1 1,474,929 391,857 26.6
2 1,468,357 385,286 26.2
3 1,452,143 373,000 25.7
4 1,340,143 346,214 25.8
5 1,243,286 325,786 26.2
6 1,140,143 299,500 26.3
7 1,044,071 276,286 26.5
8 934,357 252,143 27.0
9 818,357 229,714 28.1
10 709,500 188,714 26.6
A-53

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Table 1M2• continued, p. 2.
SSL
TOTAL
PERCENT OF
TOTAL SSL
DATE GENERATED
DISCHARGE
DISCHARGED
(1977)
SEPTEMBER (continued)
11 608,857 149,071 24.5
12 493,643 124,786 25.3
13 472,357 207,214 43.9
14 464,429 255,571 55.0
15 462,714 301,286 65.1
16 456,500 294,214 64.5
17 481,071 295,429 61.4
18 577,000 301,643 52.3
19 697,143 307,643 44.1
20 802,571 312,071 38.9
21 925,571 322,000 34.8
22 1,031,643 333,429 32.3
23 1,150,214 341,857 29.7
24 1,273,786 349,214 27.4
25 1,394,786 356,929 25.6
26 1,479,714 347,143 23.5
OCTOBER
5 1,639,286 281,786 17.2
6 1,648,286 320,000 19.4
7 1,649,214 396,500 22.4
8 1,640,429 410,857 25.0
9 1,640,786 475,000 29.0
10 1,674,286 524,857 31.4
11 1,633,429 520,000 31.8
12 1,632,000 520,143 31.9
13 1,620,071 561,357 34.7
14 1,600,143 550,286 34.4
15 1,568,714 511,071 32.6
16 1,570,071 511,929 32.6
17 1,575,500 514,214 32.6
18 1,557,186 532,143 34.2
19 1,543,357 510,286 33.1
20 1,520,786 462,643 30.4
21 1,505,071 407,500 27.1
22 1,486,214 387,571 26.1
23 1,464,857 342,643 23.4
24 1,431,643 317,357 22.2
25 1,435,929 317,714 22.1
A-54

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Table I—M—2. continued, p. 3.
DATE
SSL
TOTAL
PERCENT OF
TOTAL SSL
DATE
GENERATED
DISCHARGE
DISCHARGED
(1977)
OCTOBER (continued)
26 1,406,714 317,714 22.6
27 1,403,357 277,929 19.8
28 1,376,500 262,214 19.1
29 1,404,000 256,786 18.3
30 1,411,214 255,500 18.1
31 1,399,243 248,429 17.8
NOVEI2ER
1 1,405,214 217,571 15.5
2 1,399,500 225,929 16.2
3 1,420,929 290,286 20.4
4 1,396,714 337,429 24.2
5 1,410,429 339,643 24.1
6 1,430,786 319,786 22.4
7 1,459,714 293,643 20.1
8 1,490,571 298,143 20.1
9 1,499,571 298,500 19.9
10 1,517,286 302,429 19.9
11 1,560,143 202,857 19.5
12 1,552,500 304,000 19.6
13 1,545,143 298,429 19.3
14 1,541,286 272,929 17.7
15 1,533,500 254,786 16.6
1,630,357 258,143 15.8
DECEMBER
19 1,630,357 258,143 15.8
20 1,773,286 290,214 17.5
21 1,654,429 324,500 19.6
22 1,605,429 320,714 20.0
23 1,490,857 314,143 21.1
24 1,370,357 305,714 22.3
25 1,260,357 299,143 23.7
26 1,147,714 293,500 25.6
27 1,073,000 293,857 27.4
28 1,019,357 260,286 25.5
29 1,005,571 231,357 23.0
30 978,214 226,357 23.1
31 953,429 201,571 21.1
A-55

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Table I—M—2. continued, p. 4.
SSL
TOTAL
PERCENT OF
TOTAL SSL
DATE GENERATED
DISCHARGE
DISCHARGED
(1978)
JANUARY
1 953,429 201,571 21.1
2 909,929 154,000 16.9
22 1,672,714 257,500 15.4
23 1,669,929 294,857 17.7
24 1,645,571 321,429 19.5
25 1.645,786 324,714 19.7
26 1,663,071 330,929 19.9
27 1,673,571 361,143 21.6
28 1,691,786 363,571 21.5
29 1,675,143 365,929 21.8
30 1,660,929 412,171 24.8
31 1,633,286 389,143 23.8
1,638,786 346,500 21.1
FEBRUARY
1 1,638,786 346,500 21.1
2 1,642,714 311,571 19.0
3 1,642,000 290,571 17.7
4 1,269,500 266,786 16.4
5 1,614,286 260,214 16.1
18 1,389,714 202,571 14.6
19 1,381,143 215,214 15.6
20 1,364,071 227,214 16.7
21 1,346,071 236,929 17.6
22 1,314,000 239,357 18.2
23 1,373,214 252,286 18.4
24 1,373,286 253,286 18.4
25 1,453,643 254,643 17.5
26 1,486,000 252,071 17.0
27 1,495,857 246,786 16.5
JULY
31 425,429 68,071 16.0
AUGUST
1 314,143 53,357 17.0
2 196,286 36,071 18.4
3 68,714 16,857 24.5
12 43,214 8,857 20.5
A-56

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Table I—M—2. continued, p. 5.
SSL
GENERATED
TOTAL
PERCENT OF
TOTAL SSL
DATE GENERATED
DISCHARGE
DISCHARGED
(1978)
OCTOBER
31 1,000,140 157,214 15.7
NOVE ffiER
1 894,429 151,786 16.9
2 787,929 148,071 18.8
3 701,929 145,643 20.8
4 647,214 143,714 22.2
5 640,071 141,643 22.1
6 644,071 135,929 21.1
7 632,571 135,143 21.4
DECEIfflER
29 365,429 58,714 16.1
30 268,571 48,643 18.1
31 171,071 36,357 21.3
(1979)
JANUARY
1 60,214 25,214 41.8
6 76,000 44,214 58.2
7 121,286 45,429 37.5
8 185,571 47,429 25.6
9 252,286 51,429 20.4
10 322,357 54,643 17.0
A- .57

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Table I-M-3. TOTAL MONTHS ITT RAYONIER EXCEEDED THE DAILY AVERAGE
BOD PERNIT REQUIREMENT DURING JANUARY 1976 TO JUNE 1980
Source: See “Reference” Column
Permit Requirement:
300,000 lbs/day
329,000 DMR
346,000 DMR
Permit Requirement:
29,000 lbs/day
145,000 DI,
221,000 DMR
193,000 D
297,000 DMR
304,000
296,000 DMR
(1979)
JAN
FEB
MAY
APR
MAY
JUN
JUL
AUG
SEP
OCT
Permit Requirement:
29,000 lbs/day
122,000 DMR
159,000 DMR
219,000 D
206,000 DMR
227,000
282,000 DNR
151,000 DMR
84,000 D1IR
128,000
47,000 D!fl
MONTH/
MONTH/
YEAR QUANTITY REFERENCE YEAR QUANTITY REFERENCE
(1976)
JAN
MAY
(1977)
JUL
AUG
SEP
OCT
NOV
DEC
(1978)
JAN
FEB
MAR
APR
MAY
JUN
JUL
AUG
SEP
OCT
NOV
DEC
FEB
91,500
D fl
MAR
86,500
DMR
APR
30,400
DNR
MAY
44,200
D
JUN
43,200
DIIR
287,000
274,000
279,000
209,000
242,000
194,000
140,000
99,000
123,000
124,000
84,000
140,000
SOC
SOC
SOC
DMR
DMR
DMR
DMR
DMR
DMR
DMR
DMR
DMR
A-58

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(1977)
JAN 16
JUL
AUG
SEP
OCT
NOV
DEC
3—16,18—27,29—31
1—12,14—28
1—31
SOC
SOC
SOC
Soc
SOC
SOC
(1979)
JAN N/A
FEB N/A
MAR 1—31
APR 1-30
MAY 1-31
JUN 1—24,27—30
JUL 1,7,9—18,20—31
AUG 1,7,10—24,28,31
SEP 1—3,6,7,9,13,16,17,22—26
OCT 2,3,5—11
DEC 28—30
Table I-?4-4. TOTAL DAYS PER MONTH ITT RAYONIER EXCEEDED THE DAILY MAXIMUM BOD 5 PERMIT REQUIREMENT
DURING JANUARY 1975 TO JUNE 1980
Source: See “Reference” Column “N/A” = “Not Available” from DOE or EPA Region X.
YEAR/
INCIDENTS
YEAR
,
INCIDENTS
MONTH/DATES
PER
MONTh REFERENCE MONTH/DATES
PER
MONTH REFERENCE
DMR
DMR
DMR
DMR
DMR
DMR
DMR
DMR
(1978)
APR
MAY
JUN
JUL
AUG
SEP
OCT
NOV
DEC
(1976) Permit Requirement: 400,000 lbs/day
JAN 6—9,26,27 6
APR 15,19 2
MAY 1,3,7—10,12 7
JUL 9,28 2
SEP 23 1
OCT 28,29 2
NOV 24 1
1
Permit Requirement: 55,000 lbs/day
1,2,7—31 27
1,214,6—31 29
1—3,14—23,26,27,29,30 17
1—4,11,13—31 24
1-30 30
1—7,9—16,18—22 22
1—30
1—31
1—13,15—22,24—30
1—2,6,7,9—18
N/A From August 1978
N/A to February 1979,
and in June 1980,
N/A DMR’s indicate the
N/A highest maximum va-
lue for the month,
N/A not the nuiρber of
incidents, idica—
ting at least one
incident per month
is verified.
30
31
28
14
N/A
N/A
N/A
N/A
N/A
N/A
N/A
31
30
31
28
24
19
14
9
3
SOC
SOC
SOC
RWLI
DMR
DMR
DMR
DMR
DMR
DMR
DMR
SOC
SOC
SOC
SOC
SOC
SOC
SOC
SOC
SOC
(1978)
JAN
FEB
MAR
27
27
31
SOC
Soc
SOC

-------
Table I-M-4. Continued, p. 2.
YEAR, INCIDENTS
MONTH/DATES PER MONTH REFERENCE
YEAR
MONTH/DATES
INCIDENTS
PER MONTH REFERENCE
(1980)
JAN 11 1
Soc
FEB 10,13,15—26 14
Soc
MAR 1,3—11,13,15,16,19—21,25,31 18
Soc
APR 3,6,8—10,1214—16,18,20— 14
22,24
SOC
MAY 8,9,18,19,22,23 6
SOC
JUN N/A (See note page 1.) N/A
DMR

-------
Table I-M-5. TOTAL MONTH ITT RAYONIER EXCEEDED THE DAILY AVEARAGE SCS
PERMIT REQUIREMENT DURING JANUARY 1975 TO JUNE 1980.
MONTH/YEAR QUANTITY REFERENCE
(1975) Permit Requirement: 14,000 lbs/day
NOV 19,500 DNR
Permit Requirement: 11,000 lbs/day
DEC 21,000 DMR
(1976)
JAN 27,000 DNR
FEB 17,000 DMR
MAR 13,200 DMR
MAY 22,500 DMR
JUN 11,900 DMR
AUG 12,300 DMR
(1977)
AUG 25,600 DMR
(1979)
AUG (a) 55,900 D
SEP 46,400 D?
OCT 33,900
NOV 38,500 D
DEC 41,600 D
(a) State Interpretation of NPDES Permit
A-6].

-------
Table I-M-6. TOTAL DAYS PER MONTH ITT RAYONIER EXCEEDED THE DAILY MAXIMUM SCS PER}IIT REQUIREMENT
DURING JANUARY 1975 TO JUNE 1980
Source: See “Reference” Column “N/A” “Not Available” from DOE or EPA Region X
YEAR,
MONTH/DATES
INCIDENTS
PER MONTH
REFERENCE
YEAR/
MONTH/DATES
INCIDENTS
PER MONTH
REFERENCE
(1975)
(1977)
Permit Requirement:
24,000 lbs/day
JUL N/A
1
DMR
JUL 23
1
SOC
(a)
OCT N/A
1
DMR
AUG 15,22,25,29,30
11
SOC
NOV N/A
10
DMR
(1978)
Permit Requirement:
20,000 lbs/day
FEB 24
1
SOC
DEC N/A
15
DMR
MAR 7,8
2
SOC
(1976)
JUN 8,15,16
3
SOC
JAN 8—15,17—27
19
SOC
SEP N/A
1
DMR
(b)
FEB 1—3,13—15,17,18
8
SOC
NOV N/A
2
DMR
APR 18,19
2
SOC
DEC N/A
7
DMR
MAY 8—12,18,27
7
SOC
(1979)
JUN 13
1
SOC
JAN N/A
2
DMR
AUG 3,15
2
SOC
JUL 25,26
2
SOC
SEP 20
1
SOC
AUG 2,5—6,8,10,13—16,18—25,
OCT 6,19
2
SOC
28—31
22
SOC
(1977)
SEP 1—3,5—8,13,15—30
24
SOC
JAN 16
1
SOC
OCT 1,2,5—15,18—22,29—31
21
SOC
(c)
JUN 11,15,28
3
SOC
(a) State Interpretation of NPDES Permit.
(b) From July 1.978 to February 1979, no daily information is available. DMR’s indicate total violations,
without dates.
(c) Subsequent to installation and operation of secondary treatment (10—12-79), ITT recorded TSS in place
of SCS on the submitted DMR’s.

-------
Table I-M—7. TOTAL MONTHS ITT RAYONIER EXCEEDED THE DAILY AVERAGE TSS
PERNIT REQUIRZNENT DURING JULY 1977 TO JUNE 1980
Source: See “Reference t ’ Column
MONTH/YEAR
QUANITITY
REFERENCE
(1979)
AUG
55,900
SOC
(a)
SEP
47,000
SOC
DEC
41,600
SOC
(1980)
FEB
87,500
SOc
MAR
63,700
SOC
APR
60,300
SOC
MAY
47,700
SOC
JUN
52,200
DNR
(a) No data available July 1978 to December 1978.
A-63

-------
Table I-M-8. TOTAI.I DAYS PER MONTh ITT RAYONIER EXCEEDED THE DAILY MAXIMUM
TSS PERMIT REQUIREMENT DURING JIJLY 1977 TO JUNE 1980
Source: See “Reference” Colunni
YEAR/
MONTH/DATES
INCIDENTS PER
MONTH
REFERENCE
(1977) Permit
Requirement:
77,000
lbs/day
AUG
3
soc
NOV
1
SOC
(a)
(1979)
AUG 5,6,8,13,18
5
SOC
SEP 5,16,18,26
4
SOC
OCT 10
1
SOC
DEC 18—24
4
SOC
(1980)
FEB 10,13—22,27—29
14
SOC
MAR 1—10
10
SOC
APR 2—5,13,16
6
SOC
MAY 8
1
SOC
(a) No Daily Data Available July 1978 to December 1978.
A-64

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Table I-M-9. TOTAL DAYS PER MONTH ITT RAYONIER EXCEEDED THE DAILY
MINIMUM pH PER REQUIRENENT DURING JULY 1977 TO JUNE 1980
Source: See “Reference” Column
YEAR/MONTH DATES INCIDENTS PER MONTH REFERENCE
Permit Requirement: 5.0
(1977)
JUL 1,2,6—31 28 SOC
AUG 1,2,4—31 30 SOC
SEP 1—3,14—23,26,27,29—30 17 SOC
OCT 1—4,11,13—31 24 SOC
NOV 1—30 30 SOC
DEC 1—16,18—22,29—31 24 SOC
(1978)
JAN 3—16,18—27,29—31 27 SOC
FEB 1—12,14—28 27 SOC
MAR 1—31 31 SOC
APR 1—30 30 SOC
MAY 1—31 31 SOC
JUN 1—13,15—22,24—30 28 SOC (a)
(1979)
MAR 1—31 31 SOC
APR 1—30 30 SOC
MAY 1—31 31 SOC
JUN 1—24,27—30 28 SOC
JUL 1,7,9—17,20—22,27 15 SOC
AUG 8,10—13,27 6 SOC
SEP 9,17,21,23—26,29 8 SOC
OCT 5—7,26 4 SOC
(1980)
JAN 3 1 SOC
MAR 11,12,20,22 4 SOC
APR 23 1 SOC
MAY 8,10—12 4 soc
(a) No Daily Data Available July 1978 to February 1979 and June 1980 (SOC).
A-65

-------
Table I-M-lO. TOTAL DAYS PER MONTH ITT RAYONIER EXCEEDED THE DAILY
MAXIMUM pH PERMIT REQUIREMENTS DURING JULY 1977 TO JUNE 1980
Source: See “Reference” Column
YEAR/MONTH
DATES
INCIDENTS PER MONTH REFERENCE
1980
24,26
2
Soc
(a)
(a) No Daily Data Available July 1978 to December 1978.
A-66

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APPENDIX 111-A
SUNZ4ARY OF CURRENT METER
OBSERVAT IONS IN PORT ANGELES
HARBOR AND VICINITY

-------
Table 11 1-A-i. SUMMARY OF CURRENTS OBSERVED FOR LESS THAN SEVERAL DAYS
IN PORT ANGELES HARBOR AND VICINITY.
Reference S
t atiOfl
No.
Oheervatton
depth
(in)
Mean*
spe d
(in . )
g t Current+
direction
(°True toward)
Number of aerva
obeervationa period
tion
duration
(hours)
Latitude
48°N-
(minutes)
Longitude
123°W-
(minutes)
1.
Stein and Denison
0
0.081
60
13
suloner 1965
1965
0.3
0.3
7.30
7.30
24.37
24.37
(1966)
6
0.061
77
13
suniner
2.
Nash. St. Pollution
5
Unknown
Unknown
1
14-18 July 1964
1964
100.0
100.0
8.30
8.30
24.87
24.87
Control Coesnission
27
Unknown
Unknown
1
14-18 July
1964
100.0
8.30
24.87
(1967)
44
Unknown
Unknuvu
1
July
5-27-70
24.12
3.
lollefion η i .
(1971)
12
13
12
11
2
8
13
2
8
13
2
8
2
4
8
2
4
20
2
4
8
30
60
2
4
20
30
58
0.102
0.077
0.080
0.054
0.038
0.020
0.047
0.062
0.089
0.061
0.064
0.624
0.668
0.119
0.670
0.370
0.229
0.186
0.216
0.084
0.049
0.280
0.111
0.065
193
299
325
294
221
300
88
106
178
168
191
28
017
119
79
160
116
145
102
48
31
135
105
175
5
4
4
4
3
3
2
2
4
3
4
2
2
2
6
3
3
3
4
3
2
2
2
2
5-27-70
5-27-70
5-27-70
5-28-70
5-28-70
5-28-70
6-10-70
6-10-70
6-11-70
6-11-70
6-11-70
7-14-70
7-14-70
7-16-70
7-15-70
7-15-70
7-15-70
7-15-70
7-13-70
7-17-70
7-17-70
7-17-70
7-17-70
7-17-70
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
0.2
7.60
7.60
7.28
7.28
7.28
7.60
7.60
7.60
7.60
7.60
8.45
8.45
8.45
8.45
8.45
8.45
8.45
8.45
8.45
8.45
8.45
8.45
8.45
24.12
24.12
22.85
22.85
22.85
24.12
24.12
24.12
24.12
24.12
23.45
23.45
23.45
23.45
23.45
23.45
23.45
23.45
23.45
23.43
23.45
23.45
23.45

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Table IIIwA-1. Continued 1 page 2
Reference Station
No.
(N,servation
depth
(m)
Hem”
.peed
(‘. •1)
Net Current
direction
(bTrue tiward)
Number of
ob.ervattone
.ervat1on
period duration
(hour.)
Letitude
48°N-
(minute.)
Longitude
123°W-
(minute.)
3. Tollefeon Ti 2 0.555 264 2 7-23-70 0.2 8.45 23.45
(1971.) cent. 60 0.150 298 2 7-23-70 0.2 8.45 23.43
22 2 0.255 278 4 7-24-70 0.2 7.60 24.12
4 0.205 313 2 7-24-70 0.2 7.60 24.12
5 0.293 290 2 7-24-70 0.2 7.60 24.12
10 0.182 319 4 7-24-70 0.2 7.60 24.12
21 2 0.996 93 3 7-28—70 0.2 8.45 23.45
4 0.123 138 2 7-28-70 0.2 8.43 23.43
20 0.524 86 2 7-28-70 0.2 8.43 23.45
60 0.222 139 4 7-28-70 0.2 8.45 23.45
2 0.140 352 7 7-30-70 0.2 7.60 24.12
4 0.132 338 5 7-30- 70 0.2 7.60 24.12
8 0.146 295 4 7-30-70 0.2 7.60 24.12
10 0.423 317 2 7-30-70 0.2 7.60 24.12
10 Unknavn Unknoun 1 7-30-70 2.9 7.60 24.12
15 0.227 310 4 7-30-70 0.2 7.60 24.12
2 0.403 204 5 7-31-70 0.2 7.60 24.12
4 0.092 207 5 7-31-70 0.2 7.60 24.12
8 0.086 176 3 1-31-70 0.2 7.60 24.12
10 0.129 134 2 7-31-70 0.2 7.60 24.12
10 Unknoun Unknown 1 7-31-70 2.3 7.60 24.12
13 0.043 87 3 1-31-70 0.2 7.60 24.12
21 2 0.494 233 3 8-6-70 0.2 8.45 23.45
4 0.598 259 3 8-6-70 0.2 8.45 23.45
S 0.637 279 2 8-6-70 0.2 8.45 23.45
30 0.223 217 3 8-6-70 0.2 8.45 23.45
57 0.648 106 3 8-6-70 0.2 8.45 23.45
2 0.491 301 3 8—7-10 0.2 8.43 23.45
4 0.507 286 4 8-7-70 0.2 8.45 23.45
• 0.388 290 3 8-7-70 0.2 8.43 23.45
10 0.511 299 3 8-7-70 0.2 8.43 23.45
20 0.291 308 3 8—7-10 0.2 8.45 23.45
30 0.281 293 3 8—7-70 0.2 8.45 23.45
35 0.238 3)8 4 8-7-70 0.2 8.45 23.45

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Table 111-A—i. Continued, page 3
Reference — Station
No.
Thaervation
depth
(iii)
tteanW Net Currentw
apeecf direction
(! a ) ( 6 True toward)
Number of
obeervattona
Obaervation Latitude
period duration 48°N-
(hours) (minuteel
Longttude
123°W-
(mtnutee)
3. To llefson 8 11. 12 2 0.318 99 3 8-11-70 0.2 7.60 24.12
(1971) cont. 4 0.285 98 2 8-11.70 0.2 7.60 24.12
10 0.161 132 3 8-11—70 0.2 7.60 24.12
15 0.100 276 2 8-11-70 0.2 7.60 24.12
2 0.021 334 12 8-12-70 0.2 7.60 24.12
4 0.080 330 12 8-12-70 0.2 7.60 24.12
8 0.072 307 11 8-12-70 0.2 7.60 24.12
10 0.071 318 11 8-12-70 0.2 7.60 24.12
12 0.110 322 12 8-12-70 0.2 7.60 24.12
15 0.120 219 11 8-12-70 0.2 7.60 24.12
2 0.078 303 14 8-13-70 0.2 7.60 24.12
4 0.070 307 14 8-13-70 0.2 7.60 24.12
8 0.069 297 14 8-13-70 0.2 7.60 24.12
10 0.080 329 16 8-13-70 0.2 7.60 24.12
10 Unknown Unknown 1 8-13-70 13.6 7.60 24.12
12 0.082 312 16 8-13-70 0.2 7.60 26.12
15 0.149 324 16 8-13-70 0.2 7.60 24.12
11 2 0.465 107 8 8-14-70 0.2 8.45 23.45
4 0.733 112 8 8-14-70 0.2 8.45 23.45
7 0.319 70 4 8-16-70 0.2 8.45 23.45
8 0.740 112 4 8-14-70 0.2 8.45 23.45
10 0.544 114 8 8-14-70 0.2 8.45 23.45
10 Unknown Unknown 1 8-14-70 9.0 8.45 23.45
15 0.609 111 6 8-14-70 0.2 8.45 23.45
20 0.645 105 4 8-14-70 0.2 8.45 23.45
40 0.396 116 4 8-14-70 0.2 8.45 23.45
2 0.921 116 4 8-17—70 0.2 8.45 23.45
4 0.987 111 3 8-17-70 0.2 8.45 23.45
8 0.959 111 3 8-17-70 0.2 8.45 23.45
10 0.528 119 2 8-17-70 0.2 8.45 23.45
10 Unknown Unknown 1 8-17-70 1.7 8.45 23.45
15 0.549 711 2 8-17-70 0.2 8.45 23.45
20 0.505 111 2 8-17-70 0.2 8.45 23.45
40 0.665 111 2 8-17-70 0.2 8.45 23.45

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Table 11 1-A-i. Continued, page 4
Reference St.tLCII
No.
Observation
depth
(a)
Mean*
speed
(a 1)
Net CurrentW
direction
(°True toward)
Number of
observations
Observation
period duration
(hours)
Latitude
48°N-
(minutes)
Longitude
123°W-
(minutes)
3. tollefson . Il 2 0.510 91 3 8-18-70 0.2 8.45 23.45
(1971) cont. 4 0.163 129 4 8-18 70 0.2 8.45 23.45
8 0.242 123 4 8-18-70 0.2 8.43 23.45
10 0.157 140 4 8-19-70 0.2 8.45 23.45
20 0.458 116 3 8-18-70 0.2 8.45 23.45
40 0.914 121 2 8-18-70 0.2 8.45 23.45
2 0.235 294 6 8-19-70 0.2 8.45 23.45
4 0.146 289 6 8-19-70 0.2 8.43 23.45
8 0.20? 296 5 8-19-70 0.2 8.65 23.45
10 0.078 288 5 8-19-70 0.2 8.45 23.45
20 0.076 297 3 8-19-70 0.2 8.45 23.45
40 0.092 102 5 8-19-70 0.2 8.45 23.45
60 0.168 107 3 8-19-70 0.2 8.45 23.45
2 0.332 311 6 8-20-70 0.2 8.45 23.45
4 0.324 30? 6 8-20-70 0.2 8.45 23.45
8 0.274 315 6 8-20-70 0.2 8.45 23.45
10 0.308 299 6 8-20-70 0.2 8.45 23.45
10 Unknown Unknown 1 8-20-70 0.2 8.45 23.45
20 0.276 299 5 8-20-70 0.2 8.45 23.45
40 0.052 278 5 8-20-70 0.2 8.45 23.45
60 0.049 162 4 8-20-70 0.2 8.45 23.45
T2 2 0.030 359 2 8-28-70 0.2 7.60 24.12
4 0.108 334 2 8-28-70 0.2 7.60 24.12
13 0.444 341 2 8-28-70 0.2 7.60 24.12
ri 2 0.037 93 6 9-1-70 0.2 8.45 23.45
4 0.019 304 6 9-1-70 0.2 8.45 23.43
I 0.035 284 7 9-1-70 0.2 8.45 23.45
10 0.005 159 6 9-1-70 0.2 8.45 23.43
10 Unknown Unknown 1 9-1-70 6.2 8.45 23.45
20 0.176 120 6 9-1-70 0.2 8.45 23.45
40 0.305 107 6 9-1-70 0.2 8.45 23.45
60 0.323 94 4 9-1-70 0.2 8.43 23.45

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Table 111-A-i. Continued, page 5
Reference
Station
No.
?3
0S servation
depth
(us)
MeenW
speed
Net Current*
direction
(m_•1)__(°True_toward)
Number of
observations
Observa
period
tion
duration
(hours)
Latitude
48°N-
(minutes)
Longitude
123°W-
(minutes)
3.
Tollefson .
2
0.026
73
3
9-3-70
0.2
7.28
22.85
(1971) cont.
T4
4
8
10
10
10
10
10
10
10
0.173
0.173
Unknown
Unknown
Unknown
Unknown
Unknown
Unknown
Unknown
111
114
Unknown
Unknown
Unknown
Unknown
Unknown
Unknown
Unknown
3
3
1
1
1
1
I
1
1
9-3—70
9-3-70
9-29-70
9-30-70
10-1-70
11-3-70
11-4-70
11-5-70
11-6-70
0.2
0.2
4.4
6.8
7.2
3.0
5.9
5.9
3.4
7.28
7.28
7.28
7.28
7.28
7.60
7.60
7.60
7.60
22.85
22.85
22.85
22.85
22.85
22.70
22.70
22.70
22.70
*Nean current speeds and directions are hea’rt1 biased due to very abort sampling intervals.

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Table III-A-2. SUMMARY OF CURRENTS OBSERVED FOR
OR LONGER IN PORT ANGELES HARBOR
SEVERAL DAYS
AND VICINITY.
Reference Station
Observation
Mean
Net
Current
Observation
Latitude
Longitude
No.
depth
( m l
velocity
(iii a 1 )
direction
(°T toward)
period
duration
(daye)
(°N)
(°W)
1.
National Ocean
8
5
6-22-66
32
48°
13.2’
123°
40.0’
Survey,
10
5,81,136
7—15-64
4.5
48°
13.9’
123°
32.6’
Rockville, I II.
11
5,60,99
7—15-64
4
48°
11.5’
123°
33.2’
(unpublished)
12
15
16
19
20
21
22
23
30
5,42,70
5,39,64
5,27,46
5,69,114
5,43,72
5,45,74
5,23,38
5,26,45
5,62,102
4-20-63
7—20-64
4—20-63
8-10-64
4-20-63
9—14-64
3-19-65
3—19-65
6-10-64
6.5
4
4
4
4.5
6
4.5
4
4
48°
48°
48°
48°
48°
48°
48°
48°
48°
09.6’
11.2’
09.9’
13.6’
11.6’
10.9’
09.9’
06.3’
13.9’
123°
123°
123°
123°
123°
123°
122°
122°
123°
24.6’
17.3’
12.7’
08.0’
05.8’
02.2’
57.8’
58.1’
00.1’
2.
Cannon (1978)
PMEL-C
13
27
57
121
0.07
0.08
0.04
0.05
258
258
231
111
2-25-76
2-25-76
2-25-76
2-25-76
40
40
40
40
48°
48°
48°
48°
11.44’
11.44’
11.44’
11.44’
123°
123°
123°
123°
39.75’
39.75’
39.75’
39.75’
PMEL-B
16
61
125
0.27
0.15
0.17
289
295
96
2-25-76
2-25-76
2-25-76
40
40
40
48°
48°
48°
14.60’
14.60’
14.60’
123°
123°
123°
39.10’
39.10’
39.10’

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Table III-A-2. Continued, page 2
—
———
—
Reference Station
No.
Observation
depth
(iii)
Mean
velocity
(In a’i)
Net Current
direction
( 0 T toward)
Observation
period duration
(days)
Latitude
(°N)
Longitude
(°W)
3. Ebbesmeyer et al la (EPA) 5
(1979)
6-07-79 32 48° 7.5’ 123° 22.3’
4. Holbrook at .1.
(1979)
5. Pacific Marine
Environmental
Laboratory
Sandpotnt ,
Seattle, Vs.
(unpub I ished)
0.03
160
ST-8
4
0.20
243
1-02-78
44
48° 14.6’
123° 15.4’
ST-9
4
0.15
324
12-19-78
109
48° 23.3’
123° 01.5’
ST—b
4
0.22
319
12-19-77
119
48° 13.0’
122° 57.2’
ST-10
ST-li
ST-13
ST- 13
JDF 42
JDF 52
10 ,20
4,10,20
4,10,20
10,20
30,60,120
30,60
12-19-77
7-16-78
7-16—78
7-16-78
12—18-77
7-13-78
119
41
94
106
122
84
48° 13.0’
48° 14.4’
48° 14.1’
48° 14.1’
48° 13.8’
48° 14.6’
122° 57.2’
123° 05.5
122° 57 4’
122° 57.4’
122° 58.3’
122° 58.9’
C 80
4.5
0.15
205
3-30-76
15.1
48° 06.45’
122° 57.45’
C 80
C 80
21
67
0.08
0.18
175
93
3-30-76
3-30-76
15.1
15.1
48° 06.45’
48° 06.45’
122° 57.45’
122° 57.45’
C 81
C 81
4.5
27
0.12
0.04
164
20
10-29-75
10-29-75
11.3
22.8
48° 10.93’
48° 10.93’
122° 56.07’
122° 56.07’
C 82
4.5
0.35
78
10—18-75
15.1
48° 11.23’
123° 09.50’
C 82
C 82
C 83
C 83
C 83
21
91
4.5
21
131
0.34
0.16
0.12
0.07
0.23
73
98
180
198
95
10-18-75
10-18-75
10-18-75
10-18-75
10—18-75
15.1
15.1
15 1
15.1
15.1
48° 11.23’
48° 11.23°
48° 14.90’
48° 14.90’
48° 14.90’
123° 09.50’
123° 09.50’
123° 12.10’
123° 12.10’
123° 12.10’
C 8
4.5
0.13
93
10-14-75
15.1
48° 08.15’
123° 17.45’
C 89
2.7
0.23
4
9-02-75
15.1
48° 10.62’
123° 32.52’
C 89
4.5
0.20
325
9-02-75
15.1
48° 10.62’
123° 32.52’

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Table III-A-2. Continued, page 3
S
Ref
erence
St
ation
No.
Obeervat
depth
(a)
ion
Keen
velocity
(a e 1 )
Net Current
direction
(°T toward)
Obeerva
period
tion
duration
(daye)
Latitude
(°N)
Longitude
(°V)
.
3.
continued
C
C
C
C
C
Τ
C
C
C
C
C
90
90
90
90
90
90
90
90
90
90
94
21
21
61
61
107
107
144
107
144
144
7
0.31
0.23
0.10
0.13
0.18
0.12
0.14
0.04
0.10
0.07
0.02
245
251
167
231
73
65
68
83
62
75
109
9-02-75
10—07—75
9-02-73
10—07—75
9-02-75
9—22—75
9-02-73
10-07-75
9-22-75
10-07—75
2-19-76
19.0
11.3
19.0
11.3
19.0
13.3
19.0
11.3
30.6
11.3
19.0
48° 13.85’
48° 13.85’
48° 13.85’
48° 13.85’
48° 13.85’
48° 14.03’
48° 13.85’
48° 13.85’
48° 14.03’
48° 13.85’
48° 08.13’
123° 33.43’
123° 3343’
123° 33.43’
123° 33.43’
123° 33.43’
123° 33.55’
123° 33.43’
123° 33.43’
123° 33.55’
123° 33.43’
123° 25.00’

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APPENDIX 111-B
OBSERVAT IONS OF WATER PROPERTIES
IN PORT ANGELES HARBOR
AND VICINITY

-------
rab1e Ill-B-i. OBSERVATIONS OF WATER PROPERTIES IN PORT ANGELES
HARBOR AND VICINIP?
Reference Parameters
Number
of
Number of
Observation Remark.
observed
surveys
stations
period
per survey —
1. Vestley (1956.) Temp., Sal., 8.0., 1 31 11 Sept. 1956 Referenced in Collies
S.V.L. (1970) but data not
Included.
2. Ve.tl.y (1956b) Temp., Sal. 8.0., 1 40 16 Oct. 1956 Referenced in Collie.
5.11.1.., 8.0.8. (1970) but data not
Included.
3. Peterson and Gibbs Temp., Sal., 8.0., 7 23 26 June- Physical and dbemIcal
(1957) 5.11.1.. 24 Sept. 1957 data tsk.n in conjunc-
tion with bacterial
surveys.
4. charnell (1958) Temp., Sal., 8.0., 21 23 24 Aug. 1956
5.11.1.., p11 19 Mar. 1958
S. ott (1961) Temp., 8.1., D.0., 1 30 28 Nov.-
5.11.1.., sulfite., 7 Dec. 1961
volatile solids
6. St.in j. Sal., 8.0., S.V.L., 4 53 Unknonn Data later included in
(1962, 1963) pH, water transparency Stein and Denison (1966).
7. Callavay . Temp., Sal., 8.0., 14 18 Sept. 1962- Also described by
(1965) 5.11.1.., pH, vater Jan. 1964 Bartsch e j. (1967)
transparency and Wash. St. Pollution
Control Coauiilssion
(1967).

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Table 1 1 1-B-i. Continued, page 2
—
R.T rence
Parameters
observed
Number of
surveys
Number of
station.
Observation Remarks
period
per survey
8. Stein and Denteon Sal., 0.0., S.V.L., Unknown 53 1961-1966 Data from Stein et al
(1966) p1 1, water transparency (1962. 1963) incLuded.
9. Wash. St. a. Temp.. Sal., 0.0., 9 10 July 1963- Physical and chemical
Pollution Control S.W.L.I pH, water June 1966 data taken in cotijunc-
Comaiuton (1967) transparency tioti with plankton
ecology surveys.
b. Temp., Sal., D.0., 13 6 April-May Physical and chemical
S.V.L., pH, total 1964 data taken in conjunc-
sulfide. tion with Juvenile
salman bioassay..
c. Sal. 1 LV I .. 19 12 May 1963- Physical and chemical
August 1964; data taken in con junc-
Nov. 1964 tion with oyster larvae
bioassay.. Also
described by Paulik
(1966).
10. 0.5. Dept. of temp., Sal., 0.0., 1 26 23 July 1970 Bacteria survey also
Interior (1970) S.W.L., pil conducted.
11. Collias (1970) Tamp., Sal., 0.0., several varies 1932-1966 md cl to physical and
S.V.L. , nutrients chemical hydrographic
data taken by the
University of Washington,
Wash. St. Dept. of
Fisheries, and the
Pacific Oceanograpli Ic
Group, Canada.

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Table 111-B-i. Continued, page 3
Observation Remarks
Reference Parameter.
Number
of
Number
observed
survayl
stations
per survey
period
12. Anpitarte (1972) Temp., Turbidity, 1 3 18-19 Jan. 1972 Stations repeated
Zinc., Sodium ten time, each.
13. Aspitarte and Swats Temp., 0.0., pH, 3 varies 13 t. 1971- Hydrographic data
(1972) volatile solids 21 Jan. 1972 taken in conjunction
with a study of
Croun Zellerbach’s
sludge beds.
14. Pins (1972) Yemp., 0.0., S.W.L., 1 6 23 Peb. 1972
pH, Turbidity,
total solids, s6nc.
IS. Envtrcsncentst (1972.) Temp., 8.1., 0.0., 1 30 3-4 Nay 1972 Bacteria survey also
Protection 8.11.1., pH, Turbidity, ponducted.
Agency
16. invircumental (l972b) Temp., Sal., 0.0., 1 30 31 ( t.- Bacteria survey al.o
Protection 8.11.1., p0, Turbidity 1 Nov. 1972 conducted.
Agency
17. Enviri .nta1 (1974) Temp., Sal., 0.0., pH, 1 12 23 April 1973
Protection 8.11.1., total
Agency su.pended saudi
ii. Moore (1976) Temp., Sal., D.0., 1 6 22-27 May 1976 Live boa bioassay
8.11.1., pH, dissolved also conducted.
total suit ides, turbidity
19. Young and Corwaek Temp., 0.0., p 1, sinc 1 10 15 June 1976
(1976)

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Table 111—B-i. Continued, page 4
Reference
Parameters
observed
Number of
surveys
Number of
stations
per survey
Observat ion
period
Remarks
20.
Fagar ren (1976)
9.1., D.O., S.W.L.,
pH, turbidity
2
varies
17-18 June
and
17-18 Aug. 1979
Stations were repeated
usually seven times
par survey.
21.
Denison and Pagergren
(1977)
Temp., DO., S.V.L.,
pH
unknown
unknown
unknown
22.
Fagergren and Rodgers
(1977)
Temp., D.O., 8.11.1..,
pH
1
22
18-20 May 1977
23.
Enviroonsntal
Protection
Agency (1979)
Temp., Sal., 3.11.1..,
pH, 8.0.0., nutrients,
fluorescence
2
varies
5-9 June 1979
unpublished, oyster
larvae bioassay
also conducted
24.
Enviroemental
Protection
Agency (STalEr)
a. University of
Washington
Temp., Sal., 0.0.,
S.W.L.. nutrients
unknown
62
1962-1964
STORET is the EPA’s
Water Quality Data
Storage and Retrieval
System. Data is
unpublished.
b. Wash. St. Dept.
of Fisheries
unknown
20
1970-1972
c. Wash. St. Dept.
of Ecology
unknoim
5
1968-1979

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APPENDIX Ill-C
Plan views of surface SSL and salinity
in the harbor from surveys by Callaway
et al. (1965). Winds and tides were
obtained from the National Climatic
Center, Ashville, North Caroline and
National Ocean Survey (1962,1963,1964),
respectively.

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.‘
N.
,
I $
w

,
1I11II1h1I \
s
#yp’
. ,
I I
‘Ii
IL 41 i11iUIti
c) WIND
3
2
0
—I
d) TIDE
4’5’6’7’9 ’
SEPTEMBER 1962
8
Figure 111-C-i.
Plan view of SWL (a) and salinity (b) in the Harbor on 9 September 1962.
Wind (c) and tide (d) data are sham f or S days prior to and including
the survey date. Dashed lines indicat, length of survey.
20
15
I0
5
0
5 ,
6
E
0
w
I d
a-
(I )
0
z
E
I—
I
0
Id
I
Id
0
I—

-------
E
a
U
U
A.
U )
a
z
E
I .-
U
Q
Figure III—C—2.
Pin via of MIL (a) aS saiisity (b) is tbs Marbor a 3 Psbruary 1963.
Wind Cc) and tids (d) data ars stra in for 3 days prior to and including
tb. survay dats. Dasb.d tins. indicats lsngth of surny.
JANUARY 1963 FEBRUARY

-------
15
5
0
S
I0
Is
3
2
o
—I.
II
N-f S II
* II
Ii
I,
-‘-- “ir’ ” w r . -’ ’
II
I I
‘I
II
I’
c)WIND I’
II
d)TIDE H
3 I 4
5
6
MARCH 1963
7
B
Figure III-C-3.
Plan view of SWL (a) and salinity (b) in the Harbor on a March 1963.
Wind Cc) and tide (d) data are •honn for 5 days prior to and including
the survey date. Dashed lines indicate length of survey.
20
10
t U)
E
0
w
Lu
a-
U)
0
z
E
I
t&i
I
Lu
0
F-

-------
6
E
0
I d
Id
0
U,
2
E
I-
Id
0
I-
Figur€. III—C-4.
Plan ,i of IL (a) and saltatty (b) to die Iarbor on 17 April 1H3.
Wind Cc) and tide Cd) data are shonn for 5 days prior to and tocludini
the survey date • Dashed lines indicate leu th of survey.
APRIL 1963

-------
E
CD
U
U
a-
(I)
CD
z
E
I—
I
U
I
U
CD
I -
I.
I II
*
I I
\\ YV 1II15 { ‘ r
I
I,
I’
c)WIND ‘I
IS
I0
5
0
5
so
15
d)TIDE
APRIL 1963
Figure ill—C—S. Plan view of SVL (a) and salinity (b) in the Harbor on 18 April 1963 (.orntng).
Wind (c) and tide (d) data are .h vn for 3 day. prior to and including the
survey date. Dashed lines indicats length of survey.
‘3
‘4
15
16
‘7
18
20

-------
N S

r’
I
I
I
I
..,..J/// ii i 1 IIii
I
c) WIND
I
d) TIDE
13 ‘ 14’ 15
APRIL
16 ‘ I ? • 8
1963
Plan view of SWL (a) and salinity (b) in the
(afternoon). Wind (c) and tide (d) data are
and includin$ th. survey date. Dashed lines
aerbor is ie April 1N3
sham for 5 days prior to
indicate l.n th of s &rv.y.
20
IS
10.
5,
0
I0
IS
3
a
0
—a
c
E
a
I d
Id
0.
U.,
0
z
E
I-
Id
0
I-
-Figure
IIi—C—6.

-------
E
C
(a
(a
0 -
U)
0
z
E
I-
I
0
(a
0
F-
Figure III-C--7.
Plan iev of IL (a) and salinity (b) in the Harbor on 26 June 1963.
Wind (c) and tide Cd) data are sham for 5 days prior to and including
the survey date. Dashed lines indicate length of survey.
20
I6
I0
S
0
S
I0
IS
JUNE 1963

-------
S
£
0
I d
Id
a.
U)
0
z
E
I-
Id
0
I-.
Figure III-C—8.
laa vi., of IL (a) and salinity (b) in the Harbor on 27 July 1963.
Wind (c) and tide (d) data are shone for 3 days prior to and tecludin
U i. survey date. Dashed lines indicate length of survey.
JULY 1963

-------
15
I0
5
0
S
I0
I 5
3
2
0
—I
E
Q
I d
Id
U)
0
2
3
E
I.-
I
0
U
I
U
0
I—
Figure III—C—9. 21.. wt of IL
Vtnd Cc) and tid.
th. surysy dat..
(a) and salinity (b) in tb. larbor on 30 August 1q63.
(d) data are •honn for 3 days prior to and tnc1udin
Dash.d line. indicate l.n th of ourvey.
20
AUGUST (963

-------
lb
10
5
0
N— -—3

•.pp,g.rg,tv•)
II
I I
II
II
II
• 1 I
/, 1 . J//I4 .. /L y ivr
II
I I
10
I
I
c)WIND
I
a
0
d)TIDE
3
-u -- U 5
SEPTEMBER 1963
Figure uI—C-b.
Plea view of IL (a) and salinity (b) in the Rarbor on S Sept..b.r 1963.
Wind Cc) and tide Cd) data are shown for 5 days prior to and inc1udin
the survey date. Dashed line. indicate length of survey.
4;
E
0
U
U
0

-------
0
5
I0
IS
c) WIND
4;
E
w
U
If)
0
z
E
I-
I
I . ,
U
I
U
0
I -
Figure I l l—C —il.
3
2
0
—I
d)TIDE
-fr
24 25 26 27 28 29
OCTOBER
963
Plan view of IL (a) and salinity (b) in the Harbor on 29 October 1963.
Wind (c) and tide (d) data are shown f or 3 days prior to and including
the survey date. Dashed lines indicate length of survey.
_____ I I
IS N..—4 -s
I I
(0
Ii
. , 1 d.,,r\\ tL\

-------
0
5
I0
‘5
3
2
—I
‘
I
I

I
#-s
9 ... . i1llh1iUii&
\t
c) WIND i_i____
d)TIDE
DECEMBER 1963
Figure III—C-12,
Pt .. vi.. of IL (a) aM saltaity (b) to ha larbor os 10 D.cs.b.r 1q63.
ViM (c) aM Uds (d) data ar. .ha.a for S days prior to aM Lncludtui
th. sarv.y dat .. Da.hM hose thdtcats 1.a th of survey.
20
$5
$0
5
E
a
I d
Id
0
U)
0
z
E
I-
Id
Q
I-

-------
c) WIND
d)TIDE
7 8
JANUARY 1964
Figure III—C—13.
4
Plan vtsw of mit (a) and salinity (b) in th. Harbor on 9 January 1964.
Wind (c) data sham for survey date only; tide (d) data shown for 5 day.
prior to and including the survey date. Dashed lines indicate length
of survey.
5
6
9
15
Io
5
I0
15
‘In
E
0
L u
Lu
U)
0
z
E
I .-
I
Lu
0
I—

-------
APPENDIX III-D
AERIAL PHOTOGRAPHS OF PORT ANGELES HARBOR
AND VICINITY

-------
Table III-D-l. AERIAL PHOTOGRAPHS OF PORT ANGELES
HARBOR AND VICINITY
Source
1. U.S. Army Corps of
Engineers
2. Environmental Protection
Agency
3. ITT Rayonisr, Inc.
4. Evans-Bamilton, Inc.
Type of Photograph
black - white
a. multispectral
b. mult .spectral
color
a. color
b. color
c. color
Observation Period
yearly surveillance flights
1970, 1972, 1974
April - July 1973
March - April 1979
June - August 1976
April 1978
August 1978
.lune 1979
A-96

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APPENDIX V-A
TOXICITY TESTS, THODS AND EFFECT PARAMETERS

-------
Appendix V-A TOXICITY BIOASSAY METHODS
Standard Methods: Standard methods for the toxicity testing of
aquatic organisms have been reviewed and outlined by Sprague (1969,
1970, and 1971), APHA (1976), and the Committee on Methods for
Toxicity Tests with Aquatic Organisms PA l97 . Walden (1976) has
specifically reviewed the toxicity of pulp mill effluents and the
corresponding measurement procedures. Woelke (1972) and Woelke
and Cardwe].1 (1979) have developed a receiving water bioassay for the
detection of pulp mill effluents in marine waters which utilizes
much of the standard testing methodology; these will be
discussed separately under receiving water bioassays.
The general categories of toxic effects which are commonly used to
refer to the type of stimulus applied to an organism and the response
exhibited are presented in Table V-A—i. Several of the terms are
synonymous. However, fish bioassays of pulp mill effluents have
generally been designed to indicate acute and/or sublethal toxicity.
The techniques generally used for conducting toxicity tests are
outlined in Table V-A-2. The static technique with or without
replacement of the toxicant has been utilized most freqently with
pulp mill effluents. Table V-A-3 outlines the terminology utilized
to exoress the results of toxicity tests. This report will generally
limit the expression of toxicity to use of the terms LC5O, ECSO
and LT5O.
Toxicity is a biological response which when quantified in terms
of the concentration of the toxicant, can constitute the basis for
a bioassay procedure. To produce meaningful results, bioassay pro-
cedures require carefully controlled test conditions. For pulp
and paper effluents, bioassays usually use an indigenous species of
fish, with death as the response criterion.
Pulp mill effluents are complex wastes (i.e., not all constituents
or concentrations chemically known) where the toxicity of the con-
stituents can only be measured by bioassays. The bioassay of pulp
A-98

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Table V-A-i. GENERAL CATEGORIES OF TOXIC EFFECTS
ACUTE — Involving a stimulus severe enough to bring about a response
speedily, usually within two to seven days for fish.
SUBACUTE - Involving a stimulus which is less severe than an acute
stimulus, which produc a response in a longer time,
and may become chronic.
CHRONIC - Involving a stimulus which is lingering or continues for a
long time, often used for periods of about one tenth of
the life span or more.
LETHAL - Causing death, or sufficient time to cause it, by direct
action.
SUBLETHAL - Below the level which directly causes death.
CUMULATIVE - Brought about, or increased in strength, by successive
additions at different times or in different ways.
DELAYED - Symptoms do not appear until an appreciable time after
exposure; often the response is triggered by occurrence
of some other stress.
SHORT-TERM - Acute but more indefinite.
LONG-TERM - Chronic but more indefinite.
A-99

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Table V-A-2. TECHNIQUES GENERALLY USED FOR CONDUCTING TOXICITY TESTS
STATIC TECHNIQUE - Test solutions and test organisms are placed in
test chambers and kept there for the duration of the test.
STATIC RECIRCULATION TECHNIQUE - Similar to the static technique
except that each test solution is continuously circulated
through an apparatus to maintain water quality by such means
as filtration, aeration, sterilization and returned to the test
chamber.
STATIC RENEWAL TECHNIQUE — Similar to the static technique except
that the test organisms are periodically exposed to fresh test
solution of the same composition usually once every 24 hours
by transferring the test organisms from one test chamber to
another.
CONTINUOUS FLOW or FLOW-THROUGH TECHNIQUE - Test solutions flow into
and out of the test chambers on a once-through basis for the
duration of the test. Two procedures can be used: (1) large
volumes of the test solutions are prepared before the beginning
of the test and these flow through the test chambers and (2)
fresh test solutions are prepared continuously or every few
minutes in a toxicant delivery system.
A— 100

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Table V-A-3. TERMINOLOGY USED FOR EXPRESSING RESULTS OF TOXICITY TESTS
LC5O — Median lethal concentration of a toxicant in solution which
is lethal to 50% of the test organisms.
EC5O - Median effective concentration of a toxicant in solution at
which a response other than death occurs to 50% of the test
organisms.
LD5O - Median lethal dose of a toxicant within the organism which
is lethal to 50% of the test organisms.
ED5O — Median effective dose of a toxicant within the organism at
which a response other than death occurs to 50% of the test
organisms.
LT5O — Median lethal time. Used for mortality time in fixed concen-
trations.
ET5O — Median effective time. Used for response time other than
death in fixed concentrations.
TLm TLm, TL 5 , TL5O - Median tolerance limit. Term used primarily
by U.S. pollution biologist. Equivalent numerically to LC5O.
LL5O - Median lethal level. For tests which yield mortality data
where neither concentration nor dose applies, e.g. tests with
temperature.
EL5O — Median effective level. For tests which use a response
other than death where neither concentration nor dose applies,
e.g., tests with temperature.
ILC5O — Intermittent lethal concentration of a toxicant in solution
which is lethal to 50% of the test organisms during intermit-
tent exposure tests.
Other Terminology - Usually used to describe the concentration at
which toxicity ceases or the point beyond which 50% of the
population can live for indefinite time:
Incipient lethal level
Ultimate median tolerance limit
Lethal threshold concentration
Median threshold concentration
Asymptotic lethal concentration
Asymptotic threshold concentration
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mill effluents poses special problems. The low concentration of
toxicants require high concentrations of the effluents in bioassay
test solutions. The high oxygen demand of these test solutions neces-
sitates oxygenation to maintain adequate oxygen levels for fish
respiration during the test. These conditions are highly conducive
to depletion of the unstable toxic constituents. Compounding these
problems is the depletion of toxicants due to their uptake by the
test fish.
The most widely used organism for Pacific Northwest pulp and paper
mill effluent testing is the rainbow trout ( Salmo gairdneri) , because
of the availability of this species at suitable small sizes for test-
ing throughout most of the year. Other salmonids. (Pacific salmon)
are more difficult to acquire at certain times and appear to be
more sensitive to effluent toxicants (Walden 1976).
The use of rainbow trout poses problems in the method of test
solution aeration. Rainbow trout usually require dissolved oxygen
(DO) of >8.0 mg/i to avoid stressful conditions in the test solution.
DO values less than this could create combined or synergistic, respir-
ation - toxicity problems. Walden (1976) reconunends a DO concentra-
tion of 9.0 — 10.2 mg/l at a standard 15.0± 1°C temperature.
Aeration of test solutions reduces toxicity through vola-
tile loss of unstable toxic effluent constituents. Foaming of the
test solution, one indication of volatile loss, can be created when
diffused air or oxygen is used. Walden and McLeay (1974) determined
that volatile loss could be minimized by introducing air through a
hypodermic needle. The fine bubbles would be adsorbed in the test
solution. This would comply with the recoimnended standard of 9.0 —
10.2 xng/l and minimize reduction in the toxicity.
Standard Methods (APHA 1976) recommends DO levels of >5.0 mg/i.
This concentration is quite low for adequate salmonid testing. The
Environmental Protection Agency (EPA) published standard methods for
effluent testing in 1975 and recommended that test solutions should
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not be aerated, thus attempting to closely simulate the actual effluent
discharge results in the environment.
The pH must be maintained between tolerance limits of 6.0 — 9.0
to support test salmonids. Rainbow trout are best suited to waters
having a pH of 7.0 - 8.0. Walden (1976) referred to a common prac-
tice of neutralizing effluent to a pH of 7.5. Numerous studies
(Walden 1976, Leach and Thakore 1974, Leach and Thakore 1977)
have shown that effluent is more toxic at a pH of 6.7 than at 7.3.
The APHA (1975) recommends a pH of 7.0 - 8.0. The EPA (1975)
recommends that no effluent neutralization should occur, again
attempting to duplicate environmental toxicity more, closely.
One of the mechanisms of fish mortality in static bioassays is the
absorption of toxic constituents by the test organism. In order
to control this accumulation in a 96—hr bioassay, specific loading
densities (biomass) per testsolutionare required. Walden eta]. (1975)
found that 0.5 g/l loading density limited depletion of toxicants.
Sprague (1969) determined loading densities should be maintained at
0.33 - 0.50 g/l. If greater densities are,used then faster adsorp-
tion occurs and the 96—hr toxicity appears to be less than that
of lower densities.
Test effluent samples are usually too warm for immediate bioassay
with fish, thus samples must be allowed to cool. The samples must
be collected in opaque containers and filled in stoppered vessels
to exclude air (Walden and McLeay 1974). Samples must be stored at
low temperatures no longer than four days (Walden 1976) to avoid
anaerobic degradation of the effluent (production of hydrogen sul-
fide). Since large volumes of effluent are required for multiple
static bioassays, this can create transportation problems when
off-site bioassays are conducted.
Mortality occurring in the control tests is also an important con-
sideration. Every effluent test series must have a control, con—
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sisting of 100% dilution water. The control bioassay is used to
determine if factors other than effluent toxicity cause responses
in test animals (i.e., high zinc concentrations in dilution water,
diseased fish, etc.). If control mortalities exceed 10% the test
must be rerun (Walden 1976, APHA 1976).
Washington Department of Ecology Bioassay Methods: In August 1974,
pulp and paper mill effluent bioassay methods were developed by
the Washington Department of Ecology, Department of Fisheries,
Department of Game, National Air and Stream Improvement Council,
Northwest Pulp and Paper Association, and representatives of pulp
and paper mills. These standard methods were to be used by pulp
and paper mills conducting National pol lutjonDiScharge Elimination
System (NPDES) required bioassays.
Ten test fish per test aquarium (recommended by the DOE)weretobe
any salmonids, or the equivalent that showed comparable sensitivity
to the effluent tests. The DOE requires APHA (1976) recommendations
of loading densities (biomass) not to exceed 1.0 gil. The largest fish is not
to exceed 1.5 times the length of the smallest fish per test aquarium.
Aeration and pH, discussed previously, are specified by DOE standards
in a different manner. The DOE states thatpH canbe adjusted within
the range of 6.5 - 8.5. The dissolved oxygen concentration must
exceed 5.0 mg/i at 15.0+ 2.0C. The dissolved oxygen standard also
suggests a greater temperature variance may also be allowed. Aera-
tion is required to be either the inverted glass funnel or the 3-nun
I.D. glass tubule method. Through these approaches there is thought
to be a minimization of the loss of volatile toxicants. The large
bubbles produced by the tubules, when controlled to 2 to 3 per
second, cause volatiles to “roll” around the larger surface area.
In the case of diffused air, volatiles adhere to the smaller bub-
bles causing volatile dissipation. The funnel or tubule method
also keeps the test solution gently mixed, thus avoiding strati-
fication of test effluent (since effluent is usually denser than the
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dilution water in freshwater). According to R. Burkhalter, DOE,
(personal cominun.tcation)alterations in pH and aeration shown above were made
to determine effluent toxicity characteristics aside from those
related to BOD and pH.
Effluent samples, if cooled, are required to be stored at 40 no
longer than 48 hours. Samples may be collected by either the
grab (instantaneous filling of container) or the composite (series
of smaller grab samples over time (usually 12 to 24 hours)) methods.
The DOE states that any mortality in controls requires a rerun of
the test. This is a stringent requirement, as opposed to Walden
(1976) and the APHA (1975) which recommend acceptance at <10 percent
mortality.
Other DOE requirements are 1) stock fish acclimation mortality
must not exceed 5 percent, four days prior to testing, 2) water
for acclimation and dilutions must be fresh water, and 3) test
aquaria recommended are 5 gallon wide-mouth, cylindrical, glass
jars, capable of containing at least 10 liters of test solution.
NPDES Bioassays
According to NPDES permits for both Crown Zellerbach and ITT Ray-
onier, interim bioassay monitoring programs were to be established
to determine the toxicity of the primary treated mill effluent for
each mill. The permit states that 100 percent fish survival must
occur in 65 percent effluent, using methods described by the DOE.
This criterion was determined by Servizi et al. (1962) and adopted
by the International Pacific Salmon Fisheries Commission. It
formerly applied to pulp and paper mills on the Fraser River, B.C.,
and was adopted by the Canadian government and the Washington
State DOE. Since that time other standards based on LC5O concen-
trations have been adopted by the British Columbia government
(LC5O :90 percent effluent). In actuality, the 100 percent survival
in 65 percent effluent was made because there was no accurate LC5O
data at the time to arrive at a standard. According to Servizi
(personal communication) this standard was established in a short
period of time.
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APPENDIX V-B
OYSTER BIOASSAY METHODS

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Appendix V-B OYSTER LARVAE BIOASSAY
General Approach: The Washington State Department of Fisheries
has assessed the acute toxicity of the marine waters of the State
to bivalve mollusc larvae since 1961. This biomonitoring has been
conducted at least annually or more frequently and has utilized the
larvae of Pacific oyster ( Crassostrea gigas ) and two species of
native clams (native little neck clam, Protothaca staininea , and
horse clam, Tresus nuttalli ) as test organisms. The method of
testing has involved measuring in the laboratory the effects of
samples of natural receiving waters on the shell development and
mortality of these organisms during development from the fertilized
egg to the fully-shelled, 48—hour-old veliger. These bioassays
have been referenced to the following selected water quality para-
meters: Pearl-Benson Index (PBI), an index of the concentration
of certain (unidentified) hydroxylated aromatic compounds specific-
ally and the concentration of pulpmill effluents and wood and plant
leachates generally (Barnes et al., 1963); salinity; dissolved
oxygen; pH; total ammonia-nitrogen; chlorophyll a; and the age
of the seawater sample at the time that testing commenced.
Dr. Charles Woelke began development of the oyster larvae bioassay
procedure for testing the acute toxicity of materials during the
late 1950’s and began monitoring application in the marine waters
of the State shortly thereafter. This work was in response to
long—standing allegations by the Pacific Northwest commercial
oyster industry that the Olympia oysters ( Ostrea lurida ) and
Pacific oysters were being decimated by local pulpmill wastes.
The Pacific oyster larvae was selected because the species is
commercially important, sensitive to low concentrations of pulp—
mill effluents (Gunter and McKee, 1960; Woelke, 1960a), and
amenable to testing in the laboratory. The rapidity of measuring
sensitive responses and a minimal requirement for elaborate
equipment except for a supply of flowing seawater were additional
positive aspects of the method.
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Up to the late 1960’s the toxicity data accumulated for the Pacific
oyster larvae generally were considered specific to this species
and inapplicable to understanding the broader and more important
question of effects of pulpmill effluents on marine biota. But
as evidence accumulated indicating the almost extraordinary
sensitivity of these larvae to pulpmill effluents relative to other
biota (Woelke, 1960a, 1960b, 1960c, 1960d, 1972; Holland et al.,
1960; Washington State Enforcement Project, 1967; Wilson, 1972;
Cardwell et al., 1977a), the potential of the Pacific oyster
larvae as an indicator organism was recognized. Walden (1976)
has termed the extraordinary sensitivity of this bioassay
“anomalous”.
Mi indicator species is sufficiently sensitive to toxic substances
that its response or lack of response should reflect similar
responses in at least some of the resident aquatic biota. However,
the concept of the indicator species is frequently defined more
narrowly to include only indigenous organisms. The responses of
an indicator may include increased viability of a few species in
specified zones of pollution or dysfunction of an organism when
exposed to a substance in a toxicity test.
The receiving water bioassay is not well known. Kobayashi (1974a,
1974b) has used this procedure with sea urchins in Japan. Cummins
et al. (.1976) has performed similar testing with oyster larvae in
Washington. Use of the Pacific oyster larvae as the test organism
has been viewed with skepticism by some. This is because the
Pacific oyster is exotic to North inerica and larvae are rare
in situ because the adults reproduce irregularly and only in a
few regions of the colder waters of the Northeast Pacific.
However, the presence of the embryonic stages of most marine
organisms in the plankton is ephemeral, and it could be argued
that their use in a bioassay at times of the year or in areas
where they failed to occur naturally also would be unrepresentative.
Continued testing has revealed that the larvae of many bivalves
including Pacific oyster are fairly uniform in sensitivity to
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diverse toxic substances such as pulpmil]. effluents (Woelke, 1972),
oil refinery and aluminum smelter effluents (Woelke et a].., 1971),
anionic surfactants of the linear alkylate sulfonate type (Cala—
brese and Davis, 1967; Granino, 1972), pesticides (Davis and Hidu,
1969; Liu and Lee, 1975), and metals (Calabrese, 1972; Calabrese
and Nelson, 1974). Bivalve larvae are frequently comparable if
not more sensitive to pollutants than fish and macroinvertebrates
(Woelke, 1972; Roberts et al., 1975).
Laboratory bioassays and toxicity tests frequently are disparaged
as a valid method for predicting effects in situ since such para-
meters as dilution, water quality, test environment, and the form,
phase and structure of the substance being tested are unrepre-
sentative of the complex and dynamic conditions present in situ .
One method of minimizing these recognized limitations, while
retaining the biological criterion of toxicity and the attributes
of laboratory testing, is to bioassay the receiving water.
Historically, receiving water bioassays have been accomplished
with live boxes, but their use has been constrained by the
mechanics of establishing, maintaining and observing the test
organisms. Such bioassays are more practical when bivalve or
other microinvertebrates constitute the test specimens because
the specimens are small and possess low metabolic requirements
that exert negligible effects on water quality (i.e. dissolved
oxygen, ammonia). Hence, in the receiving water bioassay with
Pacific oyster larvae, small volumes of receiving water can be
brought to the laboratory, inoculated with several thousand
fertilized eggs, held for 48 hrs in a controlled environment during
which the embryos develop into fully-shelled veliger larvae, and
then subsampled to measure one or more of their responses.
The receiving water quality biomonitoring program conducted by
WSDF was designed to ensure that the quality of the marine and
estuarine waters assured the survival, growth and reproduction
of the resident biota. This program also intended to define
A—l 09

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long-term trends in water quality, detect pollution, monitor
pollution abatement and assist in the development and validation
of criteria for toxic substances and effluents.
Receiving waters were sampled by scooping water from the surface
with plastic containers or by collecting surface and sub-surface
samples with a Van Dorn bottle. The samples were then transported
by air to the WSDF Point Whitney laboratory on Hood Canal where
toxicity testing commenced the same day (within 8 hrs). The
laboratory was supplied with a constant supply of high quality
uncontaminated seawater. A review of the general approach and
considerations of the oyster larvae bioassay follows.
In order to conduct a bioassay on a desired date and assure good
quality test specimens, gaxnetogenetically-active adults must be
held at elevated temperatures (5-10°C above ambient) in the
laboratory in flowing seawater for a few days to a maximum of
6 weeks to stimulate maturation of the gametes. Spawning the
oyster and clam species was accomplished by raising the water
temperature 5-10°C above the conditioning temperature and adding
sperm from a sacrificed male. Spawning usually occurs within
60 minutes. Progeny from a single male—female pairing was used
to minimize variability in stock quality and larval responses
(Woelke, 1968). After selecting the group of progeny manifesting
the most normal initial development (i.e., using fertilization
success and the symmetry of the embryos when they round up and
commence cleavage as criteria), the spawn density is determined
and several thousand embryos introduced into each one liter
polypropylene test vessel. Embryo densities range from 15,000 to
35,000/1, with a mode of 35,000/1 and are held constant for a
given test. Test containers are held for about 48 hrs at 20°C
in a water bath or incubator to allow development into the full-
shelled (D-shaped) veliger. Since Pacific oyster embryos normally
require 22.-28 hrs at 20°C to develop into a fully shelled veliger
this duration and timing is the effective period of exposure for
the shell development criterion (24 1w). The mortality criterion
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is reflected in the entire period (48 hr). Mortality usually
occurs prior to completion of shell development because fewer
specimens rather than empty—shelled larvae are encountered at the
end of the test. Large numbers of treat nents (75-105) are
normally tested in duplicate; therefore, practical exposure periods
may range from 40—54 hr.
After about 48 hr a subsample of the larvae is removed and pre-
served in a vial with buffered formalin following the subsampling
methods of Loosanoff and Davis (1963) and Woelke (1972) for the
period 1961 through 1974 and the modification by Cardwell et a l. ,
(1978)
Abnormal shell development and mortality are the two larval
responses measured. They are determined by examining and enumerating
the subsample of larvae using a light microscope. Abnormal larvae
lack a fully-developed bivalve shell. The percentage abnormal
shell development statistic is calculated as follows:
% abnormal shell — No. abnormal larvae (100)
development No. abnormal + normal larvae
Mortality is determined indirectly as shown:
% ortaiit — ( No. larvae introduced - No. surviving (100)
m — No. larvae introduced
The number of larvae introduced is relatively uniform because a
constant volume containing a known density or larvae is added to
each container. Between 1961 and 1974, the number of larvae
introduced was based on one or two estimates of spawn density and
the volume of spawn added to each container. The actual number of
test specimens depended upon the accuracy of the spawn density
estimates and the accuracy and precision of the pipetting.
Beginning in 1975, the accuracy of estimated test specimen density
was improved by collecting and later counting subsamples of embryos
from the first and last three containers ixmnediately after com-
mencing the test. The precision of the mortality statistics prior
A—ill

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to 1975 were no doubt reduced, however; the general trends would
be expected to remain the same.
The responses of all treatment larvae are evaluated relative to
those of the larvae exposed to samples of fresh, untreated sea-
water. The number of control replicates always equal 10% of the
total number of treatment replicates in order to gain a precise
estimate of control response. Special treatment of samples may
be included as well as “carry along controls” which are used to
verify whether samples were exposed to perturbations during the
interval between collection and testing.
In the course of data analysis there were cases where larval
abnormality could not be assessed because all the larvae died and
decomposed prior to reaching the shelled stage. In order to
facilitate statistical analysis and data interpretation and to
minimize data gaps all dead larvae were considered abnormal. In
cases where no larvae were observed, larval abnormality was
indexed as being 100%. There are problems with this arbitrary
decision and it may be desirable to use the “ecological mortality”
statistic of LeGore (1974), which considers only the total
number of normal larvae in the sample, and pools the abnormal
larvae with the mortalities. This problem did not affect the data
collected from the Port Angeles region.
The equations for calculating the abnormal development and
mortality percentages for a single test container were presented
above, however; the mean response of all replicates in a treatment
is usually desired. These means are weighted for the abnormality
criterion and unweighted (simple arithmetic mean) for the mortality
criterion. The weighting for abnormality is for the total number
of normal and abnormal larvae in the sample,
—l —l —l
= (n.X.) (Zn.l) + (.n.X.) (En.,2) . . . . (n X ) (En k)
where:
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= No. of abnormal and normal larvae in the th
replicate
= proportion of abnormal larvae in the th replicate
= sum of abnormal and normal larvae for all
replicates constituting a treatment (k) or control
group
Weights are necessary because numbers of surviving larvae vary
within and between replicates and the percentage abnormality
commonly increases in conjunction with a decrease in the total
number of surviving larvae.
In the statistical analysis it is necessary to correct the treat-
ment responses for that of the controls when the latter exceed a
certain percentage. Correction is performed with Abbott’s formula
(Finney, 1971):
Corrected = (100) ( Treatment response, %) — (icontrol response, % )
response, % 100 - (i control response, %)
It is assumed that increased control responses belie sensitivity
to toxicants, and tests in which control responses exceed an
arbitrarily derived 10% are commonly regarded as invalid (Committee
on Methods for Toxicity Tests in Aquatic Organisms, 1974), and
corrections are usually not applied (Stephan, 1977). However, it
remains very difficult to detect “sick” fish or oyster larvae in
control responses and until an association between the level of
control response and organismic sensitivity to stress is established,
it is prudent to correct for the control response to avoid bias.
There are no guidelines defining the level of control response
requiring correction, however; and empirical study of the problem
suggested Abbott’s formula be involved at a control response of
6%.
A variety of statistical tests (ANOV, covariance analysis, and
appropriate multiple comparison tests) are used to determine if
increased larval abnormality or mortality are significantly above
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the controls at a probability of 0.05, Bivalve larvae respond
in typical sigmoid fashion with increasing toxicant concentrations.
This curve can be straightened and relationships between dependent
and independent parameters characterized with classical probit
(Finney, 1952, 1971) and logit (Ashton, 1972) methods. Simple
transformations and least squares regression solutions are satis-
factory to approximate the relationship between dependent and
independent parameters.
Toxicity maps have been generated (Cardwell and Woelke, 1979) to
indicate the generalized marine water quality of the State and to
indicate general degradation or improvement. The maps rank the
magnitude of abnormal development and mortality when larvae are
incubated in receiving waters for each location sampled. All
responses are corrected for controls. When samples were taken
from depth the highest response between surface and depth was
plotted. The maps indicate locations causing 5-19%, 20-49% and
greater than 50% abnormal development and mortality of larvae at
one or more depths. This classification scheme is largely an
arbitrary effort to protray magnitude of effect. As a general
criterion, a larval abnormality in excess of 5% in a treatment,
was usually significant. More recent testing has indicated that
the “no effect” concentrations are 3—10% above the control for
the abnormality criterion and greater than 15% above the control
for the less precise mortality criterion.
A—1l4

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APPENDIX VI-A
TOTAL PHYTOPLANKTON (CELLS/LITER) SAMPLED AT Oin ND 50m DEPTH
FOR STATION 2

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APPENDIX VI-A
TOTAL PHYTOPLANKTON (CELLS/LITER) SAMPLED AT OM AND 50M DEPTH
FOR STATION 2
Source: Chester et al. 1978
Chiorophyta (Green Algae): Misc. Green spp. - 600
ηyanophyta (Blue-Green Algae): Misc. Blue-Green Algae - 4252
Euglenophyta (Euglenoids): Misc. Euglenoids — 1214
Microflagellates : Misc. Microflage].lates spp. — 687, 877
Chrysophyta (cocolithophorids, diatoms etc.):
Dictyocha fibula - 524
Ebria Tripartita - 870
Coccolithus pelagicus - 22
Misc. Chrysophyte spp. — 200
Pterosperma sp. - 5
Misc. Coccolithophorid spp. - 572
__________ ________ C. similis — 10,201
C. subsecundus — 50
C. teres — 50
Cocconeis scutelluxn - 6
Cocconeis pp . — 17
Coscinodiscus angstii - 160
C. asteromphalus - 167
C. centralis — 141
C. curvatulus - 46
C. excentricus — 687
C. g ranii - 10
C. lineatus — 131
C. marginatus - 40
C. nitidis — 30
C. ocusus - iridis - 20
C. radiatus — 210
C. stellaris — 10
C. wailesii — 6
Misc. Coscinodiscus spp. — 100
Ceratulina bergonii - 1012
Diatoms
Amphiprora g gantea s.s.
sulcata - 17
Asterionella japonica - 6655
Actinoptychus undulatus - 499
Asterionella spp. — 6400
Bidduiphia longicruris - 11
Bacteriastrum delicatulum — 40
Chaetoceros affinis — 7173
C. approximatus - 360
C. brevis — 6833
C. compressus — 18,667
C. concavicornis — 3357
C. constrictus — 9324
C. debilis — 2008½
C. decipiens - 2312
C. di ymus - 4146
C. gracilis — 566
C. laciniosus — 720
C. radicans — 7091
C. secundus - 825
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Appendix VI-A. continued, page 2
Diatoms
Misc. Hyalchaete chaetocerus
spp. — 39,285
Corethron hystrix — 610
ηylindrotheca c].osterium -. 8060
Diploneis spp. — 17
Ditylum brightwellii — 1609
Eucalnpia zoodiacus — 24
Fragilariopsis spp. - 401
Granunatophora spp.
Licmophora spp.
Leptoηylindrus danicus - 1057
L. niinimus — 112
Melosira sulcata — 32,815
Nitzschia delicatissixna - 2316
N. longissima — 3979
N. pungens - 1800
N. seriata — 3194
Nitzschia spp. - 411
Navicula directa - 12
N. distans - 40
Pleurosigma spp. — 38
P. formosum — 6
Rhoicosphenia curvata — 17
Rhizosolenia delicatula — 144
R. fragilissima - 361
R. hebetata F. Semispina - 150
R. setigera - 624
R. simplex — 420
R. stolterfothii — 2942
Skeletonema costatuin — 1,237,606
Stephanopyxis njpponica - 30
Stephanopyxis spp. - 40
Synedra spp. — 1140
Thalassionetna nitzschiodes -
16.686
Thalassiosira aestivalis — 8192
T. bioculata - 250
T. condensata - 8170
T. decipiens - 2647
T. eccentrica — 120
T. lineata - 620
T. nordenskioldii — 17,016
T. pacifica — 2387
T. polychorda — 1883
T. rotula — 14,917
Misc. Thalassiosira spp. — 18,040
Thalassiothrix frauenfeldii - 90
Tropidoneis antartica poly - 120
Misc. Centric diatoms — 465
Misc. Pennate diatoms - 7073
yrrophyta dinoflagellates :
Axnphidinium spp. 207
Ceratium fusus - 129
Dinophysis acuta - 210
Dinop ysis spp. — 503
Misc. Dixioflagellates — 121
Exuviella spp. - 182
Glenodinium danicum - 440
Glenodinium spp. - 27
Gonyaulax — 38
yrodinium spp. - 330
Oxytoxum spp.. - 62
Peridiniales — 429
Peridinium cerasus - 220
P. conicum - 20
P. depressum — 1102
P. discoides — 2350
P. granii - 60
P. micrapium — 40
P. minisculum — 43
P. pη .1ucidum - 60
Peridjnjuin spp. — 1239
Prorocentrum gracile — 36
A— 117

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APPENDIX VI--B
SALTWATER MARSH VASCULAR PLANTS FROM DUNGENESS SPIT

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APPENDIX VI-B
Table VI-B-l. SALTWATER MARSH VASCULAR PLANTS FROM DUNGENESS SPIT
Common Name Scientific Name
Big-Head Sedge Carex macrocephala
Tree Lupine Lupinus arboreus
Dunegrass* Elymus inollis
Water Smattwe d Polygonuin ainphibium
Creeping Spike_Rush* E].eocharis palustris
Sea—Rocket Cakile edentula
Canadian Sandspurry Spergularia canadensis
American Bulrush* Scirpus americanus
Annual Beard—Grass Polypogon monspeliensis
Lilaeopsis Lilaeopsis occidentalis
Salt Grass* Distichlis spicata
Yellow Cress Rorippa islandica
Nootka Rose Rosa nutkana var. nutkana
Gumweed Grindelia integrifolia var.
macrophyl la
Pacific Silverweed Potentilla pacifica
Silver Burweed Axnbrosiachamissonis var.
M pinnati secta
Creeping Bentgrass* Agrostis alba
Quack Grass Agropyron repens
American Vetch Vicia americana
Cattail Typha latifolia
Yarrow Achillea millefolium
Pickleweed* Salicornia virginica
Salt Marsh Dodder Cuscuta salina
ArrOwgrass* Triglochin maritimum
*Conunon
A—li 9

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APPENDIX VI-C
PERCENT RELATIVE ABUNDANCES OF DOMINANT ICHTHYOPLANRTON TAXA
COLLECTED BETWEEN ANGELES POINT AND DUNGENESS BAY FOR NTPC
BETWEEN MARCH & MAY 1978

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APPENDIX VI-C
Table VI-C-l. PERCENT RELATIVE ABUNDANCES OF DOMINANT ICHTHYOPLANKTON TAXA COLLECTED
BETWEEN ANGELES POINT AND DUNGENESS BAY FOR NTPC BETWEEN MARCH & MAY 1978
Source: NTPC 1979
SpeCies
IA
3,
lB
4 March

2A 28
3A
4A
48
IA
I I I
16,17 Mar
t.il . • n
2A 213 SA
ch
IA
.18
IA
29
18
,3O
St.i
2A
Ma
t ion
28
rch
3A
4A
48
Buttersole
0
0
00
0
0
1)
6
2
I) 0
0
Ii
0
0
0
0
0
0
0
2
l.ng lish sole
0
0
11 0
0
0
0
0
2
0 0
4
2
14
6
5
0
7
5
6
II
Crccnlings
0
0
0 0
0
0
8
0
0
0 7
I)
0
4
5
0
0
0
0
0
Pacific herring
0
37
21 23
IS
2
23
41
41
35 43
(2
8
IC,
9
7
33
8
19
14
19
Pacific sandlances
101)
27
0 3$
38
0
I)
0
4
0 0
3
0
0
23
11
17
13
7
23
20
Pacific tomcod/PaciIic cod ’
0
0
0 0
0
0
0
0
0
0 0
0
0
0
0
0
0
2
0
0
1)
Poachers
0
0
00
0
0
1)
0
8
07
I
33
5
6
6
0
4
I V
Pricklehacks (Lyconecte.. sp.)
0
0
1) IS
0
2
8
Ii
0
0 4
10
1)
I)
4
I
0
Il
5
1
0
Rockfishos
0
18
II 0
0
4)
8
If.
8
4) 4
I
3
I I)
33
28
31
40
16
8
Rocksole
0
0
0 0
0
0
0
0
0
00
0
0
0
0
0
0
0
0
0
0
Sand sole
0
0
0 0
0
0
0
6
0
0 0
0
1
3
2
2
0
2
0
-------
Table VI-C-l. Continued, page 2
Butter sole
Lnglish sole
Creeni I ngs
Pacific herring
Pacific sandlances
Pacific tomcod/Pj ilic ud
Poachers
Pricllcb. icks ( L cunecte sp.)
Rocifi shcs
Rod sole
Sand sole
Sculpins ( Artediu . pp.)
Slender sole
Snail fishes
Starry flounder
Unidentified gunnel
Unidentified l1rieI1t b.i k
tinident i lied ctil pi
halle)e Iwltod
0thcr
000024 2
6 5 4 2 2 2 <1
o 1) 0 0 0 0 (1
14 19 21 13 35 29
6 c ii 6 Il i .1
‘ I 5 2 2 5 2
2 ii 0 I 0 0 
-------
APPENDIX VI—D
DISTRIBUTION OF SUBTIDAL CLAMS, CLAM SHELL DEPOSITS, HARDSHELL
CLAM TRANSECTS AND MAJOR CLAMBEDS
FROM PORT ANGELES TO DUNGENESS BAY
-------
Log Booming
WET WEIGHT IN GRAMS / SAMPLE
k\1
I• 1
400 - 700
> 700
Figure VI-D-1.
DISTRIBUTION OF SUBTIDAL COMMERCIAL CLAMS
IN PORT ANGELES HARBOR
)
Source: Goodwin and Westley 1970
-------
Log Booming
Figure VI-D- -2. DISTRIBUTION OF SUBTIDAL NON—COMMERCIAL CLAMS
IN PORT ANGELES HARBOR
Source: Goodwin and Westley 1970
WET WEIGHT IN GRAMS/SAMPLE
___ — 0-100
— 100-400
_____ — 400 —700
IT I—>700
ci
)
-------
Log Booming
Figure VI-D-3. DISTRIBUTION OF CLAM SHELL DEPOSITS
IN PORT ANGELES HARBOR
Source: Goodwin and Westley 1970
DRY WEIGHT IN GRAMS/SAMPLE
k\i1 -0-500
—500-1000
______ — 1000 -1500
L 1—>1500
3
(
-------
Figure VI-D-4.
LEGEND FOR LOCATION OF HARDSHELL CLAN TRANSECTS
AND MAJOR CLAMBEDS, PORT ANGELES TO DUNGENESS
BAY (FIGURES VI-D—5 — VI-D—8)
Source: Goodwin & Shaul 1978
LEGEND
I
2 sq ft benth c sample
\ \\\\
Samples in which at least one market sized
littleneck or butter clam were found. Market
size littlenecks are 35 mm or larger total
shell length. Market size butter clams are
60 mm or larger total shell length.
Water depth contours calculated from zero tide
Shore line
Locations of major clam beds; population esti-
mates given in Table VI-D-I.
A—12 7
-------
I S •’ __
2
3
i&o
2 J O
Port Angeles Harbor
14

‘24
‘31
30’ CONTOUR
I
17
F,
Figure VI-D-5. PORT ANGELES HARDSHELL CLAM TRANSECTS
Source: Goodwin and Shaul 1978
-------
00 flfl )00 3000 4000 0
Strait of Juan de Fuca
‘C L
GREEN POINT
I
I
Figure VI-D-6. GREEN POINT HARDSHELL CLAM TRANSECTS
Source: Goodwin and Shaul. 1978
-------
1000 fl0 3000 4000 5020
‘p •7
9
8
12
io
1’)
0
‘13
Figure VI-D-7. DUNGENESS SPIT AND JAMESTOWN CLAM TRANSECT
Source: GoOdWifl & Shaul 1978
3
-------
1000 2000 3000 A000 5000
6’ CONTOUR
/
/
/
/
Figure VI-D-8. DUNGENESS CLAM TRANSECTS
Source: Goodwin and Shaul 1978
DungefleSS Bay
I-I
L J
]
-------
Table VI—D—l.
CLAM DENSITY AND SUBSTRATE TYPE:
PORT ANGELES HARBOR
Source: Goodwin & Shaul 1978
Port Angeles
Harbor
Figure
VI-D-5
Location &
figure no.
Station
no.
Water
depth
ft.
Market size
cla”s s . t.
11 sizes/
sg.ft.
Substrate type 8 cover
Butter
Vt
eneck
Horse
•N
WT:
N
wt.
No.
Wt.
2
3
4
5
6
7
8
9
10
•11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
32
33
34
35
36
37
38
39
40
41
42
43
44
45
46
47
48
49
so
7
6
12
11
18
62
22
62
27
70
43
25
19
37
14
49
31
20
60
41
14
75
61
44
30
15
44
12
63
56
50
32
29
19
12
10
53
46
34
26
29
17
14
16
35
18
13
16
0.00
0.00
0.00
0.25
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
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
0.44
0.00
0.25
0.00
0.00
0.00
0.11
0.00
0.85
0.73
0.29
0.40
0.06
0.62
0.35
0.00
0.0
0.0
0.0
hO
0.0
0.0
0.0
0.0
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
1.5
0.0
0.5
0.0
0.0
0.0
0.5
0.0
4.0
2.0
1.0
0.5
0.5
2.0
1.5
0.0
0.0
0.0
0.0
1.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
2.0
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
5.0
0.0
0.0
3.0
3.0
0.0
2.5
3.5
7.0
2.5
0.5
3.5
1.5
0.5
0.00
0.00
0 • 00
0.03
0.00
0.00
0.00
0.00
0.00
0.00
0 • 00
0.00
0.00
0.00
0.17
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
0.40
0.00
0.00
0.10
0.20
0.00
0.14
0.31
0.58
0.11
0.01
0.24
0.18
0.03
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
1.5
0.0
0.0
0.0
0.0
0.0
0.0
1.0
0.5
0.5
0.0
1.0
0.5
0.0
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
0.66
0.00
0.00
0.00
0.00
0.00
0.00
0.52
0.17
0.28
0.00
0.27
0.22
0.00
mud, shell, wood debris
sand, gravel, shell
mud, sand, shell
mud, pea gravel, shell, wood
chips
sand, wood chips
mud
fibrous sludge, mud, wood
chips, logs
mud
fibrous sludge, mud, wood
chips, logs
mud
mud
fibrous sludge, mud
mud, gravel, shell
fibrous sludge, mud, shell
fibrous sludge, pea gravel.
gravel, boulders, hardpan
fibrous sludge, mud, wood
chips
fibrous sludge, mud, shell
fibrous sludge, gravel.
boulders
mud, shell
mud, pea gravel, boulders
fibrous sludge, mud, sand,
pea gravel, shell
mud, shell
wd, sand, boulders, shell
mud, sand, pea gravel
fibrous sludge, mud, gravel,
pea gravel
mud
mud
fibrous sludge, mud
fibrous sludge, mud
mud
sand, wood chips
mud, sand
mud, sand, shell
fibrous sludge, mud, sand,
shell
mud, pea gravel, boulders,
shell
fibrous sludge, mud, shell
mud, pea gravel, boulders,
shell
mud, sand, shell, wood chips
mud, sand, gravel, boulders
gravel, boulders
mud, pea gravel, boulders,
shell
fibrous sludge, mud
mud, pea gravel, gravel,
boulders, shell
gravel, boulders
fibrous sludge, pea gravel,
gravel, boulders, shell
mud, pea gravel, gravel,
boulders
pea gravel, gravel, boulders
-pea gravel, boulders
pea grayel qrave1 , boulders
A-132
-------
Table VI-D—2.
CLAM DENSITY AND SUBSTRATE TYPE: GREEN POINT
Location &
figure no.
Station
no.
Water
depth
ft.
Market size
AU slzes/
Substrate type 8 cover
clams/s ft.
4$ter L tti’i i [
E •• E WE
sg.ft.
No. W
Green Pt. 1 27 0.0 0.00 2.5 0.24 1.5 0.26 gravel, boulders
2 22 2.0 0.80 0.0 0.00 0.5 0.26 mud, sand, gravel, pea gravel
19U 3 39 0.0 0.00 0.5 0.02 0.0 0.00 pea gravel, gravel
VI—D—6 4 34 1.0 0.29 5.5 0.25 0.0 0.00 pea gravel, boulders, hardpan
5 36 3.5 1.07 7.0 0.44 0.0 0.00 pea gravel, boulders
6 30 1.0 0.40 7.5 0.62 0.5 0.01 pea gravel, boulders
7 27 0.0 0.00 1.0 0.07 0.0 0.00 pea gravel, gravel, hardpan
8 32 4.0 1.06 2.0 0.12 0.0 0.00 sand, pea gravel, boulders
9 30 1.5 0.47 1.5 0.09 0.0 0.00 sand, pea gravel, boulders
10 26 0.5 0,06 1.0 0.06 0.0 0.00 mud, gravel
11 25 1.0 0.29 0.5 0.03 4.5 0.81 mud, gravel, boulders
12 30 0.5 0.20 4.0 0.31 0.0 0.00 gravel, boulders
13 26 0.5 0.22 1.0 0.06 1.5 0.06 gravel, shell, hardpafl
14 24 2.5 0.72 0.5 0.03 2.5 0.77 mud, gravel, boulders, har ,an
15 18 4.0 2.20 0.5 0.06 2.5 0.44 mud, pea-gravel, gravel,
boulders
16 30 4.0 1.18 5.5 0.30 0.0 0.00 gravel, boplders
17 22 0.0 0.00 0.0 0.00 0.0 0.00 mud, pea gravel, gravel.
boulders
18 21 0.5 0.14 0.5 0,00 0.0 0.00 sand, gravel, hardpan.
boulders
19 37 0.5 0.12 0.5 0.01 0.0 0.00 sand, pea gravel, gravel
20 —— 3.0 1.17 4.0 0.26 0.0 0.00 pea gravel, gravel
21 25 0.0 0.00 0.0 0.00 0.0 0.00 sand, gravel, shell, hardpan
22 35 0.0 0.00 0.0 0.00 0.0 0.00 solid rock outcropping
23 28 0.5 0.07 7.0 0.37 0.0 0.00 mud, gravel, shell, boulders
24 24 1.3 0.59 0.0 0.00 2.5 0.74 mud, gravel, boulders
25 24 1.0 0.38 0.0 0.00 0.0 0.00 mud, pee gravel, gravel,
boulders
26 21 1.0 0.25 0.0 0.00 0.5 0.21 mud, pea gravel, gravel.
boulders
27 31 1.5 0.32 0.0 0.00 0.0 0.00 sand, gravel, shell, hardpan
28 31 4.0 1.00 1.5 0.09 0.0 0.00 sand, gravel, pea gravel
29 25 1.5 0.41 0.0 000 0.0 0.00 sand, pea gravel, gravel,
boulders
30 25 0.0 0.00 1.0 0.06 0.0 0.00 sand, pea gravel, gravel,
boulders
31 34 0.5 0.17 0.0 0.00 0.0 0.00 pea gravel, shell
32 28 3,5 0.83 0.5 0.04 0.0 0.00 gravel, shell
33 27 0.0 0.00 0.0 0.00 0.0 0.00 sand, gravel. hardpan.
boulders
34 24 4.0 1.08 0.5 0.02 0.0 0.00 mud, pea gravel, boulders
35 31 2.0 0.53 0.5 0.03 0.0 0.00 pea gravel, shell, boulders
36 29 1 .0 0.29 0.5 0,04 0.0 0.00 sand, pea gravel • hardpan
37 25 0.5 0.18 1.0 0.03 0.0 0.00 pea gravel, shell, boulders
38 23 4.5 1.26 0.5 0.03 0.0 0.00 pea gravel, gravel, rock
outcropp lflgs
39 24 4.5 1.59 0.0 0.00 2.0 0.67 mud, pea gravel, gravel.
boulders
40 34 1.0 0.21 0.0 0.00 0.0 0.00 pea gravel, boulders
41 27 0.0 0.00 0.5 0.04 0.0 0.00 sand, pea gravel, shell
42 27 1.0 0.36 0,0 0.00 0.0 0.00 sand, pea gravel, shell.
boulders
43 25 0.0 0.00 1.0 0.05 0.0 0.00 pea gravel, gravel
44 21 0.5 0.19 0.0 .00 0.0 0.00 sand, gravel, shell, hardpan
45 29 2.0 0.61 0.0 .00 0.0 0.00 pea gravel, gravel
46 30 0.0 0.00 0.0 .00 0.0 0.00 sand, pea gravel, gravel
47 30 1.0 0.29 0.0 .00 0.0 0.00 pea gravel, gravel
48 24 0.5 0.22 0.0 .00 0.0 0.00 sand, pea gravel, gravel
49 19 1,0 .48 0.0 .00 0.0 0.00 pea gravel, gravel, boulders,
hardpan
50 29 1.0 0.22 0.0 .00 0.0 0.00 pea gravel, boulders
51 23 0.5 0.14 0.5 .01 0.0 0.00 pea gravel, gravel
52 25 5.0 1.50 0.5 .05 0.0 0.00 pea gravel, gravel, shell
53 22 2.0 0.61 0.5 .02 0.5 0.07
54 29 3.0 1.03 0.5 .02 0.0 0.00 pea gravel, gravel
55 24 0.0 0.00 0.0 .00 0.0 0.00 pea gravel
56 22 0.0 .00 0.0 .00 8.0 0.14 mud, sand, pea gravel, gravel,
boulders
57 29 0.0 0.00 1.0 L08 0.0 0.00 sand. gravel, boulders
Source: Goodwin & Shaul. 1978
A—] .33
-------
Table VI-D-3. CLAM DENSITY AND SUBSTRATE TYPE: DUNGENESS
SPIT, JAMESTOWN & DUNGENESS
Source: Goodwin & Shaul 1978
Location &
figure no.
Station
no.
Water
depth
ft. 11
Market size
c lams/sg.ft.
Butter Littleneck
All sl zes/
sg.ft.
Substrate type & cover
Horse
Wt.
Wt.
1E
wt,
Dungeness 1 24 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand
Spit 2 20 3.5 0.93 0.5 0.02 1.5 0.45 sand, gravel, boulders.
eel grass
Figure 3 16 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand, gravel, shell
VI—D—7 4 13 6.0 1.64 5,5 0,32 1.0 0.19 sand, pea gravel, boulders,
shell
5 19 0.0 0.00 2.0 0.15 0.0 0.00 sand, gravel. hardpan
6 8 0.0 0.00 0.0 0.00 0.0 0.00 sand, grovel
7 25 0.0 0.00 0.0 0.00 0.0 0.00 sand, gravel ,shell
8 28 0.0 0.00 0.0 0.00 0.0 0.00 sand
9 7 0.0 0.00 0.0 0.00 0.0 0.00 gravel, kelp
10 28 0.0 0.00 0.0 0.00 0.0 0.00 sand, gravel
11 8 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand
12 9 0.0 0.00 0.0 0,00 0.0 0.00 sand, gravel
13 12 0.0 0.00 0.0 0.00 0.0 0.00 sand, gravel
Jamestown 1 4 0.0 0.00 0.0 0.00 0.0 0.00 sand, eel grass
2 2 0.0 0.00 0,0 0.00 1.0 ——. sand, eel grass
. .gure 3 o.o 0.00 0.0 0.00 0.0 0.00 mud
V1D7 4 39 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand
5 40 0.0 0.00 0.0 0.00 0.0 0.00 pea gravel, gravel, kelp
6 16 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand
7 38 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand, shell, kelp
8 17 0.0 0.00 0.0 0.00 0.0 0.00 sand, pea gravel, eel grass
9 28 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand, shell
10 17 0.0 0.00 0.0 0.00 0.0 0.00 sand, shell, eel grass
11 17 0.5 0.28 0.0 0.00 0.0 0.00 sand, pea gravel, shell, kelp
12 28 0.0 0.00 0.0 0.00 0.0 0.00 sand
13 20 0.0 0.00 0.0 0.00 0.0 0.00 sand, pea gravel, shell
Dungeness 1 4 0.0 0.00 0.0 0.00 0.0 0.00 sand, pea gravel
2 10 0.0 0.00 0.0 0.00 0.0 0.00 sand, shell
. ure 3 15 0.0 0.00 0.0 0.00 0.0 0.00 sand, pea gravel, shell,
VI—D—8 wood chips
4 8 0,0 0.00 0.0 0.00 0.0 0.00 sand, wood chips
5 12 0,0 0,00 0.0 0,00 0.0 0.00 sand
6 13 0.0 0.00 0.0 0.00 0.0 0.00 mud, eel grass
7 14 0.0 0.00 0.0 0.00 0.0 0.00 sand, shell
8 4 8.0 •— 10.5 —— 1.5 mud, pea gravel, eel grass.
gravel
9 10 1.5 0.50 0.5 0.03 12.0 1.43 pea gravel, gravel, shell
10 8 0.0 0.00 0.0 0.00 0.0 0.00 sand, pea gravel, gravel
11 7 2.0 0.79 3.0 0.32 3.5 1.38 mud, sand, gravel, eel grass
12 Il 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand, wood chips
13 4 0.0 0.00 0.0 0.00 0.0 0.00 send
14 5 0.0 0.00 0.0 0.00 1.5 0.10 sand, pea gravel
15 3 1.5 0.41 10.5 0.91 0.0 0.00 sand, shell, eel grass
16 6 0.0 0.00 0.0 0,00 3.0 0.14 sand, pea gravel
17 6 1.5 0.45 1.5 0.19 1.5 0.12 mud, sand, gravel, shell,
eel grass
18 5 0,5 0.30 0.0 0.00 1.0 0.55 mud, sand, gravel, eel grass
19 7 0.0 0.00 0.0 0.00 0.5 0.19 sand, pea gravel, gravel
20 6 0.0 0.00 0.0 0.00 0.0 0.00 sand, pea gravel, gravel.
shell
21 B 0.0 0.00 1.0 0.12 15.0 3.14 pea gravel, gravel, shell,
kelp
22 —— 0.5 -—— 0.5 —— 6.0 ——— mud, pea gravel, gravel
23 5 0.0 0.00 0.0 0.00 2.5 mud, pea gravel, gravel
24 1 0.0 0.00 0.0 0.00 0.0 0.00 mud, sand
25 —— 0.0 0.00 0.0 0.00 0.00 0.00 sand, pea gravel
26 8 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, pea gravel, gravel
28 4 0.0 0.00 0.5 0.04 6.0 1.11 pea gravel, gravel, eel grass
29 11 0.0 0.00 0.0 0.00 0.0 0.00 sand, pea gravel, kelp
30 8 0.0 0.00 0.0 0.00 0.0 0.00 sand, gravel, shell
31 1 0.0 0.00 0.0 0.00 0.0 0.00 sand
32 9 0.0 0.00 1.5 0.09 hO 0.17 sand, pea gravel, gravel
33 9 0.0 0.00 0.0 0.00 0.0 0.00 gravel
A—134
-------
APPENDIX VI-E
LOCATION OF GEODUCK TRANSECTS AND MAJOR GEODUCK BEDS: ANGELES
POINT, GREEN POINT & DUNGENESS BAY
-------
Figure VI-E-1. LEGEND OF LOCATION OF GEODUCK TRANSECTS AND
MAJOR GEODUCK BEDS, ANGELES POINT, DUNGENESS
BAY AND GREEN POINT (FIGURES VI-E-2 - VI-E-4)
Source: Goodwin ].973a; Goodwin 1978;
Goodwin and Shaul 1978b
LEGEND
•
Either a 900 sq ft transect, a geoduck
sample taken with a water nozzle, or both
s ss
\\\\\\
Samples in which at least one geoduck was
observed
—————
60 ft water depth contour calculated from
zero tide
1/4-mile seaward from mean high water
Shoreline
‘ ‘
Major geoduck beds seaward of 1/4—mile lin
- Geoduck were observed but no transect
)OQS?Y’D counts were made.
A— 136
-------
1 1000 2000 3000 4000 5000
S
Strait of Juan de Fuca
15
—
ANGELES POINT
C Figure VI-E-2. ANGELES POINT AND PORT ANGELES GEODUCK CLAM TRANSECTS
Source: Goodwin 1973a; Goodwin 1978
—
—
I
/
/
I
-------
Strait of Juan d. Fuca
LI
0)
DUNGENESS
GREEN POINT GEODUCK CLAM TRANSECTS
EreVI3.
-------
1Ooo Oo3 io
Dallas Bank
I
(I •
C
‘3
PROTECTION ISLAND
——
f Figure VI-E-4. DUNGENESS SPIT AND DALLAS BANK* CLAM TRANSECTS
L *Dallas Bank transect counts not included in this text
Source; Goodwin 1978; Goodwin and Shaul 1978b
• . .
21 27
I.
, ‘23
I
‘26 25
,
\j
-------
Table VI-E-l.
GEODUCK TRANSECT TOTALS, WATER DEPTH AND SUB-
STRATE TYPE: ANGELES POINT, GREEN POINT AND
DUNGENESS BAY
Source: Goodwin 1973a and 1978
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Sand, pea gravel, boulders
Sand, pea gravel, boulders
Sand, pea gravel, boulders, kelp
Sand, kelp
Pea gravel, gravel, boulders
Gravel
Pea gravel, gravel, boulders
Pea gravel, gravel
Sand, gravel
Pea gravel, gravel, kelp
Pea gravel, gravel, boulders
Pea gravel, gravel, kelp
Sand, pea gravel
Sand, pea gravel, kelp
Pea gravel, gravel
Sand, pea gravel, kelp
Pea gravel, gravel, boulders
Pea gravel, gravel, boulders
Sand, pea gravel, gravel, boulders
Sand, pea gravel, gravel, boulders
Pea gravel, gravel, boulders
Sand, pea gravel, gravel
Sand, mud, pea gravel
Sand, pea gravel, gravel
Mud, sand, pea gravel, shell
Sand
Sand
Sand,
Sand,
Sand,
Sand
Sand, pea gravel
Sand
Pea gravel, rock outcroppings
Sand, pea gravel, boulders
Sand, pea gravel, boulders
Sand, pea gravel, gravel
Sand, gravel
Pea gravel, gravel, kelp
Sand, gravel, boulders
Sand, pea gravel, gravel, shell
Sand, pea gravel, kelp
Mud, sand, pea gravel, gravel
Mud, sand, gravel, kelp
Sand, gravel, kelp
Sand, gravel, shell, kelp
Mud, sand, gravel, kelp
(continued on next page)
I
ILocation and Station
figure number number
Adjusted
geoduck
siphon count
Water
depth
(ft)
Surface substrate condition
OingeleS POint*
.reen Point #3
0
0
0
0
0
0
0
0
27
0
0
0
114
0
0
0
0
0
50
0
0
14
259
61
159
9
70
27
95
18
0
0
11
0
0
0
100
64
0
27
55
130
7
0
11
0
27
40-47
45
35
36-38
36
47
43
38-43
47
31
45
33
45-55
28
46
16
22
43
38
22
22
36—41
43
25
42
50-51
30
30
54
34
45
45
41
26
30
43
48-50
44—48
30—35
30
45
42—45
30—32
25
40
30
45—48
gravel, boulders
pea gravel, gravel
gravel, shell
A— 140
-------
Table VI-E-l continued, page 2
Location and Station
figure number number
Adjusted
geoduck
siphon count
Water
depth
(ft)
Surface substrate condition -
ungeness Bay #4 1 0 31—36 Mud, sand
2 0 23 Mud
3 0 16 Mud
4 0 39 Mud
5 0 52 Mud
6 0 48 Mud
7 0 40 Mud
8 0 28 Mud
9 0 16 Mud
10 0 6—16 Mud, sand
11 0 36 Mud, kelp
12 0 46-50 Mud
13 22 40—45 Sand
14 0 15—20 Sand, kelp
15 6 14 Sand, eel grass, kelp
16 22 66—69 Mud, sand
17 10 44 Pea gravel, gravel, shell, kelp
18 3 46 Sand, gravel, pea gravel, shell. kel
19 338 64 Sand, pea gravel, shell
20 0 16—17 Pea gravel, eel grass, kelp
21 0 11 Pea gravel, eel grass, kelp
22 22 25—30 Sand, pea gravel
23 10 38 Sand, kelp
24 35 54 Sand, pea gravel, kelp
25 124 55 Mud, sand
26 22 35 Sand, kelp
27 3 26 Sand. kelp
28 0 15 Sand. eel grass, kelp
29 0 20 Sand, eel grass, kelp
30 3 32 Sand, kelp
31 0 48 Sand, pea gravel, kelp
32 153 65 Mud, sand
33 70 63 Sand. pea gravel
34 117 38—43 Sand
35 14 20 Sand, pea gravel, eel grass, kelp
36 23 29 Sand, pea gravel, kelp
37 175 32 Sand, pea gravel, kelp
38 183 45—57 Sand, pea gravel
39 53 37—62 Mud
40 8 17 Sand, eel grass, kelp
41 0 15 Sand, pea gravel, eel grass, kelp
42 214 52—57 Mud, sand
*Geoducks were observed but no transect counts were made in
tne area iocated north of ITT P ayonier, i’ort Angeles, 1ash.
A— 141
-------
APPENDIX VI-F
BENTHIC INVERTEBRATES
-------
Strait of Juan de Fuca
Crown
Zel lerbach
Corp.
ANGE LES
— — — —
— — — — —
KEY:
• — Benthic
Sampling
Station
Figure VI—F-1, BENTHIC INVERTEBRATE SAMPLING STATIONS IN
PORT ANGELES HARBOR, SEPTEMBER 30, 1961
Source: USD1 1967
)
-------
Strait oI Juan de Fuca
Crown
Zel lerbach
Corp.
ANGE LES
— — — — —
— - — — —
Figure VI-F-2. BENTHIC INVERTEBRATES SAMPLING STATIONS IN
THE WESTERN PORTION OF PORT ANGELES HARBOR,
JANUARY 19 — 20, 1972.
ne
Source: Aspitarte and Smale 1972
-------
12S3
12120’ i2 fl0
12 00’
l2 3 ’ d
• HABITAT CLASSIFiCATION INTP, 19791
* LITTORAL STATIONS INTP. 19791
o LITTORAL AND SUBLITTORAL STATIONS
ISIMENSTAD .1. .1.1977, NYBLADE 1978,
CROSS it. .1.1978, NYBLADE 19191
NUMBERS INDICATE SUBLITTORAL STATIONS
INTP 19791
mU..
‘ -a
U i
48’1Q
Pvotctlon
L .
Figure VI-p-3. LOCATIONS OF HABITAT TYPES, LITTORAL SITES AND SUBLITTORAL
SITES SAMPLED BETWEEN PORT ANGELES HARBOR AND DUNGENESS SPIT
-------
APPENDIX VI-G
BENTHIC, EPIBENTHIC AND PELAGIC INVERTEBRATES SAMPLED IN LITTORAL
AND SUBLITTORAL AREAS LOCATED BETWEEN PORT ANGELES HARBOR AND
DUNGENESS SPIT, WASHINGTON
-------
Table VI-G-l . BENTHIC, EPIBENTHIC AND PELAGIC INVERTEBRATES SAMPLED IN LITTORAL AND SUBLITTORAL
AREAS LOCATED BETWEEN PORT ANGELES HARBOR AND DUNGENESS SPIT, WASHINGTON
Littoral Zone (+7.0’
Phylum/Species Location collected
— —16.4
)
Sublittoral Zone (>—16.4’)
Reference
Location collected
Reference
PHYLUM CNIDARIA
Class Anthozoa
Anthopleura elegantissima M 2,4
Class Hydrozoa
M,ietinaria spp . 5,7 5
Aequorea aequorea D 3 D 3
Aurelia aurita M 3 D 3
Cyanea capillata* M 3
Unidentified Hydromedusae* D 1
Unidentified Medusa D 1
PHYLUM CTENOPHORA
Class Nuda
Beore spp. D 1,3
PHYLUM PLATYHELMINTHES
Class Turbellaria
Unidentified TurbeUaria M 2,4,5
-------
Table VI-G--l continued, page 2
Littoral Zone (+7.0’ — —16.-’’) Sublittoral Zone (>—16.4’ )
Phylum/Species Location collected Reference Location collected Reference
PHYLUM NEMERTEA
Unidentified Nemertea M 2,4,5 1 - 3, 5 — 7 5
PHYLUM NEMATODA
Unidentified Nemotoda M 2,4
PHYLUM SIPUNCULA
Unidentified Sipuncula 5,6 5
PHYLUM MOLLUSCA
Class Ainphineura
Cyanoplax dentiens M 2
Unidentified Aniphineura 2 5
Class Pelecypoda (Bivalvia)
Acila castrensjs 6 5
Adula californiensis M 2
Astarte alaskensis 3 5
Astarte spp . 2 5
Bankia setacea 1,5 5
Cardita aucicostata 1 5
Clinocardium californiensis 14 5 1,2 5
Compsomyax subdiaphana M 5
Crenella decussata D,M 2,4
-------
Table VI-G-l continued, page 3
Littoral Zone (+7.0’
Phylum/Species Location collected
— —16.4
‘)
Sublittoral Zone (>—l
6.4’)
Reference
Location collected
Reference
PHYLUM MOLLUSCA
Class Pelecypoda (cont)
Hiatella artica M 2 3 5
Humilaria kennerlyi 2 5
Lucina approximata M 5 2,3,5 - 7 5
Lucinoma annulata 1 - 3, 5 - 7 ’ 5
Macoma calcarea 1 3, 5 - 7 5
Macoma nasuta 1,2,5,6 5
Macoma pp . D,M,3,5,6 2,4,5
Musculus discors 2 5
Musculus pp . 2,5 5
Mya arenaria M 2
ysella tumida M 2 D,M,2,7 2,4,5
Mytilas edulis M 5
Mytilus spp . M 2,4,5 1 5
Nucula tenuis 5,6 5
Nuculana app . 3,5,6 5
Pandora bilirata 3 5
-------
Table VI-G-l continued, page 4
Littoral Zone (+7.0’ — —16.4’)
Phylum/Species Location collected Reference
Sublittoral Zone
(>—16.4
‘)
Location collected
Reference
PHYLUM MOLLUSCA
Class Pelecypoda (cont)
Pandora filosa 6,7 5
Pandora spp . 7 5
Protothaca staminea M 2,4
Protothacea laciniata M 5
Psephidia lordi D,1,2,3 2,4,5
Solen sicarius 2 5
Sphenia ovoidea M 5 2 5
Tellina carpenteri 1 5
Tellina modesta 1 5
Tresus capax M 4
Turtonia minuta M 5 1 - 3 5
Yoldia myalis 7 5
Yoldia scissurata 1,5 - 7 5
Order Cephalaspidea 5,6 5
Order Nudibranchja M 5 1 5
Unidentified pelecypoda M 5 1,2,5,7 5
-------
Table VI-G-1 continued, page 5
Littoral Zone (+7.0’ — —16.4’) Sublittoral Zone (>—16.4’ )
Phylum/Species Location collected Reference Location collected Reference
PHYLUM MOLLUSCA
Class Gas tropoda
Acmaea paleacea M 5
Acmaea app . M 5
Acmaea triangularis 2 5
Amphissa columbiana M 5 M,2,3,5 4,5
Calyptraea fastigiata M,2 2,4,5
Collisella asmi M 5
Collisella pelta M 2,4
Collisella strigatella M 2,4
Cylichna app . i 5
Haminoea virescens* M 3
Hermissenda crassicornus M 1
Lacuna spp . M 5
Lacuna variegata M 2,4
Littorina scutulata M 1
Littoriana sitkana M 2,4,5
Margarites helicinus 1,2 5
-------
Table VI-G--l continued, page 6
Littoral Zone (+7.0’
Phylum/Species Location collected
— —16.4
‘)
Sublittoral Zone (>—16
.4’)
Location collected
Reference
Reference
PHYLUM MOLLUSCA
Class Gastropoda (cont)
Margarites pupillus 1,2 5
Margarites spp . M 5 1 5
Meliba leonina M 1 D 3
Mitrella carinata 2,3 5
Mitrella g uldi 3,5,6 5
Mitrella spp . 5 5
U i
Nassarius mendicus 2,3 5
Nassarius spp . 5 5
Natica clausa 2,5,7 5
Notoacmea spp . M 2,4
Odostomia spp . 1,2,5 5
Olivella baetica 3 5
Olivella spp . 3 5
Polinices lewisii 6,7 5
Polinices spp . 1,3 5
Tachyrhychus lacteolum 2,5,6 5
-------
Table VI-G-]. continued, page 7
Littoral Zone (+7.0’ — —16.4’) Sublittoral Zone (>—16.4’ )
Phylum/Species Location collected Reference Location collected Reference
PHYLUM MOLLUSCA
Class Gastropoda (cont)
Thais app . M 2,4
Trichotropis cancellata 2 5
Turbonilla spp . 1 5
Opistobranchia M 5
Unidentified gastropoda 1,5,7 5
PHYLUM ANNELIDA
Class Oligochaeta
Unidentified oligochaeta D,M 2,4,5 1,2,5,6 5
Class Polychaeta
Anaites medipalpillata 1 5
Anaites mucosa 5 5
Aricidea app . 2,7 5
Clymene annandalei 1,2,3,6,7 5
Eumida pp . 1,2,3,5 5
Melinna maculata 7 5
Paraonis app . M 5 1,5,6,7 5
Paraprionospio p4nnata 1 - 3, 5 - 7 5
Unidentified polychaeta M 5 1 - 3, 5 - 7 5
-------
Table VI-G--l continued, page 8
Littoral Zone (χ7.0’ — —16.4’)
Phylum/Species Location collected Reference
Sublittoral Zone C>-.].
6.4’)
Location collected
—
Reference
PHYLUM ANNELIDA
Class Polychaeta
Family Ampharetidae
Anobothrus gracilis 1 - 3, 5 5
Unidentified Ampharetidae 1,2,5 - 7 5
Family Arenicolidae
Abarenicola spp . M 2,4
Arenicola spp . M 5
Family Capitellidae
Capitella capitata M 2,4 2,3 5
Mediomastus D,M 2,4
Notomastus tenuis M 5 5 5
Unidentified Capitellidae M 5 1 - 3, 5 - 7 5
Family Chaetopteridae
Phyllochaetopterus o1ifica 2,3,5,7 5
Telepsarus costarum 5 5
Family Cirratulidae
Chaetozone setosa 6 5
Cirratulus cirratus M 2,4
Cirratulus cirratus cingulatus M 5
-------
Table VI-G-l continued, page 9
Littoral Zone (+7.0’
Phylum/Species Location collected
— —16.4
‘)
Sublittoral Zone C>
—16.4’)
Location collected
Reference
Reference
PHYLUM ANNELIDA
Class Polychaeta
Family Cirratulidae (cont)
Tharyx multifilis 1. — 3, 5 — 7 5
Unidentified Cirratulidae M 5 1 5
Family Dorvilleidae
Dorvillea p eudorubovittata 1,6,7 5
Protodorvillea gracilis D 2,4
Family Glyceridae
Glycera capitata M 5 1,2,5 - 7 5
Family Go iadidae
Glycinde pp . N 5 1 - 3, 5 — 7
Goniada brunnea 5,6 5
Micropodarke dubia D 4
Family Lumbrineridae
Lumbrineris latreilli 5 5
Lumbrineris ! PP• 1,5 - 7 5
Lumbrineris zonata 6 5
Family Maldanidae
Euclymene spp . M 2
Unidentified Maldanidae M,2,3,6,7 4,5
-------
Table VI-G-1 continued, page 10
Littoral Zone (+7.0’ — —16.4’) Sublittoral Zone (>—16.4’ )
Phylum/Species Location collected Reference Location collected Reference
PHYLUM ANNELIDA
Class Polychaeta
Family Megelonidae
Megelona spp . 3,5,7 5
Family Nephtyidae
Nephtys cornuta 6 5
Nephtys ferruginea 1,7 5
Nephtys spp . M 5 1 — 3, 5 — 7 5
Family Nereidae
Micronerejs nanaimoensjs 6 5
Nereis limnicola M 5 1 5
Nereis paucidentata M 5
Nereis spp . M 2,5
Nereis vexillosa H 5
Platyneris bicanalicu].ata M 2,5 M,1,2,5,6 2,4,5
Unidentified Nereidae M 4,5 1,6 5
Family Obiniidae
Unidentified Obiniidae 1 5
Family Onuphidae
Diopatra ornata 5,6 5
Onuphis spp . 3,5 - 7 5
-------
Table VI-G-l continued, page 1].
Littoral Zone (+7.0’
Phylum/Species Location collected
—
—16.4
‘)
Sublittoral Zone
(>-16.4
‘)
Reference
Location collected
Reference
PHYLUM ANNELIDA
Class Polychaeta
Family Opheliidae
Ainmotrypane aulogaster 1,3,5 - 7 5
Armandia brevis M 2,4,5 M,l — 3,5,6 2,4,5
Haploscoloplos elongata M 5 1 - 3,5 - 7 5
Nainereis spp . 6 5
Travisia pupa 3,5 5
Family Owenhidae
Unidentified Oweniidae M 5 2,3,6,7 5
Family Pectinariidae
Pectinaria SEP . 2, 5 — 7 5
Family Phyllodocidae
Eteonelon M 5 1,5-7 5
Eteone pacifica 6,7 5
Eteone spp . M 5 1,6,7 5
Eulalia spp . 1 5
Phylodoce maculata M 5 2,7 5
Phylodoce spp . 1,5,6 5
Unidentified Phylodocidae M 5 1,2,5 5
-------
Table VI-G-1 continued, page 12
Littoral Zone (+7.0’ — —16.4’) Sublittoral Zone (>—16.4’ )
Phylum/Species Location collected Reference Location collected Reference
PHYLUM ANNELIDA
Class Polychaeta
Family Polynoidae
Eunoe oestedi 2 5
Unidentified Polynoidae M 5 1 - 3, 5 - 7 5
Family Sabellidae
Laonome kroyeri 3, 5 - 7 5
Megalomma splendida 5 5
Sabella crassicornis 3 5
Schizobranchia ins ignis 2 5
Unidentified Sabellidae M 2,4,5 1,3,5,7 5
Family Scalibregmidae
Unidentified Scalibregmidae 2,5,6,7 5
Family Serpulidae
Unidentified Serpulidae 1 5
Family Sigalionidae
Unidentified Sigalionidae 5 5
Family Sphaerodoridae
Sphaerodoropsis spp . 5,6 5
Family Spionidae
Boccardia spp . M 5 1,3,5 5
-------
Table VI-G-l continued, page 13
Littoral Zone (+7.0’
Phylum/Species Location collected
—
—16.4
S)
Sublittoral Zone
(>—16.4’
)
Location collected
Reference
Reference
PHYLUM ANNELIDA
Class Polychaeta
Family Spionidae (cont)
Laonice cirrata 5 - 7 5
Laonice spp . 5,6
Malacoceros glutaeus M 2,4 M 2,4
Nerine foliosa M 5 1,2 5
Polydora ligni M 5
Polydora socialis 1,2,5 — 7 5
Polydora spp . 2 5
Prionospio cirrifera M,l,2 2,4,5
Prionospio steenstrupi D,M 2,4
Spiophanes boinbyx M 5 D,l — 3,5,7 2,4,5
Unidentified Spionidae 2,3,5,6 5
Family Sternaspidae
Sternapsis fosser 5 - 7 5
Family Syllidae
Autolytus ! PP . 5 5
Exogone pp . D,M 5 D,M,1,3,5 — 7 4,5
-------
Table VI-G-l continued, page 14
Littoral Zone (+7.0
Phylum/Species Location collected
‘
—16.4
‘)
Sublittoral Zone
(>—16.4’) —
Reference
-
Reference
Location collected
PHYLUM ANNELIDA
Class Polychaeta
Family Syllidae (cont)
Odontosyllis 3,5,6 5
Streptosyllis latipalpa 6 5
yllides japanica 7 5
Syllis spp . N 2,5 3,5 5
Unidentified Syllidae M 5 1,2,5 - 7 5
Family Terebellidae
Atacuma conifer 6,7 5
Pista cristata 5 5
Pista 5 - 7 5
Terebellides stroemia 5 5
Terebellides pp . 5 5
Unidentified Terebellidae 1 - 3, 5 — 7 5
Family Tomopteridae
Tomopteris septentrionalis* D,M 1,3
PHYLUM ARTHROPODA
Class Crustacea
Order Cumacea
— Bathycuma spp . -- 6 5
-------
Table VI-G-]. continued, page 15
Littoral Zone (+7.0’ — —16.4’)
Phylum/Species Location collected Reference
Sublittoral Zone
(>—16.4
‘)
Location collected
Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Cumacea (cont)
Cumella pp . 2 5
Diastylis spp . 1 5
Eudorella spp . 1,5,6,7 5
Eudorellopsis app . 2,6 5
Leptocuma app . M 5 1,5,7 5
Leptostylis app . 1,2,3,5 5
Leucon pp . 2,6,7 5
Oxyurostylis pp . 5 5
Vaunthompsonia ! pp . 2 5
Order Amphipoda
Amphelisca gassizi* D 1
Amphelisca pugetica D 1
Amphelisca app . 1 — 3, 5 - 7 5
Axnphithoe hunieralis D 1 D 1
Amphithoe lacertosa D
Ampithoe app . M 5 1 - 3,6 5
-------
Table VI-G-1 continued, page 16
Littoral Zone (+7.0’
Phylum/Species Location collected
— —16
.4
‘)
Sublittoral Zone
(>—16.4’)
Reference
Location collected
Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Ainphipoda
Anisogammarus pugettensis M 1 M 1
Anonyx laticoxae M 3 D,M 1,3
Aorides coluinbiae 1 - 3,5 5
Aorides spp . 1 - 3 5
Argissa hamatipes 1,2 5
Atylus tridens D,M 1,3 M 3
I’ )
Caprella leviuscula* D 1
Corophium brevis M 1
Corophium spp . N 2,4 D,M 2,4
Erichthonius spp . 5 5
Harpinia pp . 1,3,5 - 7 5
Hippomidon denticulatus 3 5
Hippomidon spp . 5,6 5
Hyala frequens M 5
Me].ita californica M 5
Melita desdichada D 2
-------
Table VI-G-l continued , page 17
Littoral Zone (+7.0’ — —16.4’) Sublittoral Zone (>—16.4’ )
Phylum/Species Location collected Reference Location collected Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Amphipoda (cont)
Melita 1,2,5 — 7 2,5
Orchestoidea pugentensis D 1 D 1
Paraphoxus spp . M 5 D,M,1 - 3, 5 — 7 2,5
Parapleustes app . 2,3,5 5
Photis pp . 1,5 5
Pontogenia ivanovi* D,M 1
Pontogenia rostrata* D,M 1
Pontogenia app . M 5 1 5
Rhachotropis oculata 3 5
Synchelidium app . 1 - 3, 5 - 7 5
Trion app . 2 5
Trichophoxus pp . 5,7 5
Westwoodilla caecula* D,M 1
Weatwoodilla Spp . 1,5,6,7 5
Aoridae 1,7 5
-------
Table VI-G-1 continued, page 18
— Littoral Zone (+7.0’ — —16.4’)
Phylum/Species Location collected Reference
Sublittoral Zone
(>—16.4
‘)
Location collected
Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Amphipoda
Caprellidae M 5 1 5
Corophiidae 1,5 5
Gammaridae M 2,3,4 D,M 3,4
Hyperiidae D,5 3,5
Lysianassidae 1,7 5
I-a
Oedocerotidae 7 5
Photidae 3,5 5
Podoceridae 1 5
Stenothoidae M 5 3,5,6 5
Unidentified Aniphipoda D,M 2,5 1 - 3, 5 - 7 5
Order Decapoda
Cancer magister D,M 1,3
Cancer oregonensis D,M 1,3 M 2
Cancer productus D 1 M 4
Cancer spp . M 2,4,5
Crangon alaskensis D,M 1,3 D,M 1,3
-------
Table VI-G—1 continued, page 19
Littoral Zone (+7.0
Phylum/Species Location collected
— —16.4
‘)
Sublittoral Zone
(>-164’)
Reference
Location collected
Reference
PHYLUM ARPHROPODA
Class Crustacea
Order Decapoda (cont)..
Crangon communis 1,2 5
C angon franciscorum D,M 1 D,M 1
Crangon nigricauda D,M 13 D,M 1
Crangon stylirostris D,M 1,3 D,M 1
Discorsopagurus schmitti 2 5
Eualus avinus 14 1 14 1
Eualus fabricii* D,M 1,3
Fabia sub uadrata* D 1
Heptacarpus brevirostris D,M 1,3 D 1
Heptacarpus flexus 14 3 D,M 3
Heptacarpus kincaidi* M 3
Heptacarpus stylus M 1 14 1,3
Heptacarpus tenuissimus M 1 14 1
Heptacarpus tridens 1 4 3 M 3
Lebbeus grandimanus 2 5
-------
Table VI-G-l continued, page 20
Littoral Zone (+7.0’ — —16.4’)
Phylum/Species Location collected Reference
Sublittoral Zone
(>—16.4’)
Location collected
Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Decapoda (cont)
Oregonia gracilis 2,5 5
Pandalus danae D,M 1,3 D,M 1,3
Pandalus montagui tridens* M 3
Pandalus stenolepis* D,M 1,3
Pagurus spp . M 2,3,4,5 2 5
Pinnixa occidentalis 1 5
Pinnotheres pugettensis D,2 3,5
Pinnotheres taylori* D 3
Pugettia racilis N 1,2,4 D 3
Pugettia richii N 1 1. 5
Pugettia pp . M 5
Sclerocrangon alata* D 1
Telmessus cheiragonus M 2
Upogebia pugettensis D,M 1,5 D 1
-------
Table VI-G-l continued, page 21
Littoral Zone (+7.0’
Phylum/Species Location collected
— —16.4
‘)
Sublittoral Zone
(‘—16.4’)
Reference
Location collected
Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Decapoda (cont)
Hippolytidae spp . D,M 3
Paguridae M 5 M,2,6 4,5
Pandalidae* D,M 3
Unidentified Megalops* D,M 3
Unidentified Zoea D 1
Order Euphausiacea
Euphasia spp. M 1
Thysahoessa raschii* D 3
Order Isopoda
Ligia pallasi M 1
Limnora lignorum M 5 2 5
Pentidotea aculeata M 3
Pentidotea montereyensis M 1,3
Pentidotea resecata D,M 1 D,M 1,3
Pentidotea wosnesenskii D,M 1,3 D,M 1
Pleurogonium rubicundum 6 5
-------
Table VI-G-1 continued, page 22
Littoral Zone (+7.0’ — —16.4’) Sublittoral Zone (>—16.4’ )
Phylum/Species Location collected Reference Location collected Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Isopoda
Rocinela belliceps D,M 1,3 D,M 1,3
Rocinela propodialis D,2 3,5
Synidotea bicuspida* D 1
ynidotea laticauda 1 5
Argeia pugettensis D 1.
Exosphaeroma amplicauda M 2
Gnorimosphaeroma oregonense D,M 1,2,4,5 D,M 3
Hemigrapsus nudus M 2,5
Hemigrapsus pp . M 2,4
Idotea fewkesi D,M 1,5
Idotea rufescens* D 1
Idotea spp . M 2
Idotea wosensenskii M 2,4
Jaeropsis pp . M 5 2 5
ynidotea nodulosa 1 5
ynidotea spp . 1 5
-------
Table VI-G-l continued, page 23
Littoral Zone (+7.0’
Phylum/Species Location collected
— —16.4
‘)
Sublittoral Zone
(>—16.4
I)
Reference•
Location collected
Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Isopoda
Tecticeps p gettensiS* D,M 1,3
Epigardia M 5
Unidentified Isopoda M 5
Order Mysidacea
Acanthomysis davisi M 1 M 1,3
Acanthomysis macropsis* D,M 1
Acanthontysis nephrophthalama* D,M 1
Acanthomysis sculpta D,M 1 D,M 1
Acanthoinysis var nuda D,M 1 D,M 1
Archaeoinysis grebnitzkii* D,M 1,3
Archaeomysis maculata* D,M 3
Mysid sp D 1
Mysis oculata* D i
Neomysis rayil D,fl 1 D,M 1,3
Neomysis spp.* D 1
Proneomysis wailesi D 1 D 1
-------
Table VI-G-l continued, page 24
Littoral Zone (+7.0’
Phylum/Species Location collectect
— —16.4
‘)
Sublittoral Zone
(>—16.4’)
Location collected
Reference
Reference
PHYLUM ARTHROPODA
Class Crustacea
Order Ostracoda
Unidentified ostracoda 1 - 3, 5 - 7 5
Order Tanaidacea
Leptochelia dubia M 2,4,5 D,M, 1 — 3, 5 — 7 2,4,5
Class Insecta
Pipteran larvae spp . M 2,4
Diptera spp . M 2
Order Thoracica
Balanus cariosus M 2
Balanus glandula M 2,4
Balanus nubilus M 2
Balanus spp . M 2,4,5
PHYLUM ECHINODERMATA
Class Ophiuroidea
Unidentified Ophiuraidea M,3,5,6 2,4,5
Class Asteroidea
Evasterias troscheli D 1
Henrica leviuscula D 1,3
Class Holothuroidea
Unidentified Holothuroidea 7 5
-------
Table VI-G—l. continued, page 25
KEYS
Location Key: (Refer to Figure VI-H-1)
D = Dungeness Spit
M = Morse Creek
1 — 3, 5 - 7 = sublittoral
stations
Reference Key: 1 = Simenstad et al 1977
2 = Nyblade 1978
3 = Cross et al. 1978
4 = Nyblade ]. 79
5 = NTPC 1979
*Collected only in incidental fish townet samples;
therefore these species are considered to be
pelagic.
A—171
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Table VI—G-2. DISTRIBUTION OF MARINE LIFE ON THE PILING OF
ITT RAYONIER DOCK COLLECTED 1961, 1962, 1964,
1965, AND 1966
Source: Stein & Denison 1966
High Tide +2 to 3 ft
Zone
Mean Tide —4 to 6 ft
7one
Low Tide -8 to 10 ft
Zone
Upper Sub— —20 to 25 ft
tidal Zone
Lower Sub- —35 to 40 ft
tidal Zone
Salanus glandula
Balanus cariosus
Depth on
Piling Zone Piling
Species
Collected From the
Piling
Attached
Motile
Mean Tide
Nereis vexi].losa
Profuse growth of
Balanus cariosus
Nereis vexillosa
Pisaster ochraceus*
Balanus cariosus
Nereis vexillosa
Dense band of
Pisaster ochraceus*
Mytilus edulis
Dense growth of
Nereis vexillosa -
unidentified sponge
Pandalid—like shrimp
Metridiuzn seni le*
Thias lamelbsa*
Pododesmus machros-
Cancer oregonensis
chismus*
Pugettia gracillis
Balanus cariosus
Strongylocentrotus
Eudistylia polymorpha*
drobachiensis*
Small species of
Pisaster ochraceus*
Anemone
Euphausia pacifica in
the sponge*
Pododesmus macros-
Nereis vexillosa
chismus*
Thias lamellosa*
Balanus nubilis
Cancer oregonensis
Balanus rostratus
Pugettia gracillis
alaskensis*
Pandalid—like shrimp
Metridium senile*
Hermit crabs
Small species of
Strongylocentrotus
Anemone
drobachiensis*
Unidentified sponge
Pisaster ochraceus*
Eudistylia polymor-pha*
Arogobaccinum oregonense*
Archidoris monteregensis*
Hemigrapsus crab
Nudibranchs—2 species
Unidentified Chiton
Unidentified flatworm
Bottom
*Species collected only from the ITT Rayonier dock pilings.
A— 172
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APPENDIX VI- ! !
LOCATIONS OF BEACH SEINES AND FISH SURVEYS CONDUCTED IN THE STRAITS
-------
Figure VI-H-l. BEACH SEINING LOCATIONS ADJACENT TO THE PORT ANGELES DIVISION OF
ITT RAYONIER, INC., 1961 — 1966
Source: Stein and Denison 1966
Sample Date
October 12,1961
July 11,1962
September 3, 1964
June 29, 1965
July 26, 1965
Location
4,9,11,13,17
1,2,3,6
3,5,6,10,12,14,16
3,4,5,12
4,7,8,11,13,15,17
Sample Date
July 27, 1965
August 2, 1965
August 6, 1965
July 12, 1966
Location
4,7 ,8,ll
4,7,8
4,17
4,9,13
-------
Crown
Z&Iirbach
Corp.
P JUAN DE R ICA
S uch - Sulning Stutlon
NaUtIc& i i i is
Figure VI-H-2, BEACH — SEINING AND BIOASSAY STATIONS IN PORT ANGELES
HARBOR (USD1 1967)
H
U I
ANGELES
-------
SUp Po$nt
I-a
Cbssrv.tory Dtmgsnsss
Point
acha.ineandto .t: p1es,1977-1978
* = Tid.pool saapl.s 1977
LOCATION OF NEARSHORE AND INTERTIDM.a FISH
Figure VI-H-3. COIIDUCTED IN THE STRAITS 1976 - 1978
Source: Simenstad ot al. 1977; Cross et al. 1978
-------
APPENDIX VI-I
STREA ED AND PLOW CHARACTERISTICS OF THE
TWELVE DRAINAGES IN THE PORT ANGELES AREA
-------
Appendix VI-I
STREAMBED AND FLOW CHARACTERISTICS OF THE TWELVE
DRAINAGES IN THE PORT ANGELES AREA
(Refer to Figure VI-17)
Source: Williams et al. 1978)
The Elwha River, the largest river draining the north Olympic
Peninsula into the Strait, consists of 44.8 linear miles of
stream length in the mainstem. The Elwha Dam which forms Lake
Aldwell is located at river mile (measured from the mouth of
a tributary or stream) 4.9 and forms a total block to anadro-
mous fish migrations. Only 3.4 miles (5.5 km) of the river
below the dam is accessible to salmon and anadromous trout.
The gradient of the lower river (below the dam) is moderate
and the substrate is coarse. From the mouth of the river to
R.M. 3.0 the predominate substrate is rubble and coarse mater-
ial; however spawning riffles along cut bank areas are inter-
mixed in the area. Above R.M. 3.0 to the Elwha Dam the stream-
bed consists of boulders mixed with rubble and coarse material
with little spawning habitat. A passable diversion damn owned
by Crown Zellerbach Corp. is located at R.M. 3.4.
Dry Creek enters the Strait approximately 2.0 miles east of the
Elwha River. The mainstem is 4.8 miles with 9.6 miles of
tributaries. Since most the watershed is dry during the year,
salmon production is limited.
Nine creeks enter the Harbor or Strait between Port Angeles
and Dungeness Bay. Tumwater, Valley and Peabody have their
origins in the foothills. These three creeks flow through and
under the city of Port Angeles and have extensive culverted areas
which pose fish passage problems. Morse and Ennis Creeks have
headwaters in higher elevations while Lees Creek originates in
the foothills. These three creeks flow through suburban areas
of Port Angeles before emptying into the Strait. Ennis Creek
has culvert problems and is accessible to fish approximately
A—l78
-------
]. mile (1.6 kin) above Highway 101. The small size and low
summer flows in Lees Creek limit salmon use in this tributary.
On Morse Creek a falls section at R.M. 3.8 limits upstream
migration of anadromous fish. Bagley Creek which begins in the
foothills flows through rural and farm areas. At R.N. 0.1 a
slide has created an impassable barrier to fish. Siebert and
McDonald Creeks are two of the larger Creeks in the area. Both
creeks originate in high elevations in the Olympic National
Park. Eight miles of Siebert Creek are accessible to anadro—
mous fish. The culverts on this Creek sometimes form partial
barriers to fish. McDonald Creek is easily accessible to
fish up to R.M. 5.2 where a falls forms an impassable fish
barrier. A sand and gravel bar at the mouth of the Creek
sometimes delays upstream migrations. At R.M. 3.1 irrigation
water is diverted from the Creek.
In general, the lower portions of these nine creeks have
moderate gradients with gravel streambeds for spawning. The
stream channels are well defined and the stream bank coverage
is suitable in all areas except where high development occurs:.
The headwaters for most of the streams consist of steep
gradients, especially in the upper watershed areas.
The Dungeness River is divided into the lower mainstem (15.8
miles, 25.4 kin) and the upper mainstem (16.1 miles, 25.9 kin)
which begins above the confluence of the Gray Wolf River which
itself has 17.4 miles of stream. The gradient of the lower
Dungeness is steep throughout its length except for the lower
5 miles (8.0 kin). Below R.M. 4.0 the stream channel is stable,
and has several spawning gravel areas. From R.N. 4.0 to 9.0
the stream channel is broad, unstable and contains separations.
Gravel, rubble, coarse material are the major substrate above
R.M. 9.0 to R.M. 15.8. In this section the stream channeljs
stable, has several pools and passable cascades.
A— 179
-------
The lower mairistem flows from heavily forested mountainous
terrain to broad fertile lowlands at R.M. 10.0. Farming
and rural development occurs in this lowland area. The
lower 3.0 miles (4.8 km) of the river have setback levees
that prevent development adjacent to the water.
The upper mainstem of the Dungeness River and the Gray Wolf
River pass through mountainous terrain with steep gradients.
Below the timber line coniferous forests provide excellent
stream bank coverage. Due to the topography the stream chan-
nels are stable; however the steep gradient does not provide
much usuable spawning area where gravel is dispersed among
the predominate rubble and boulder substrate. Just above the
mouth of Gold Creek (R.M. 18.8) a falls blocks salmon access.
As a result only 3.1 miles of the upper mainstern is usable for
salmon production.
Fish are able to ascend to R.M. 9.0 on the Gray Wolf River;
however cascade sections usually confine the fish to the lower
7.0 miles (11.3 kin) on the upper mainstem.
A— 180
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APPENDIX VI-J
SALMON SPAWNING DATA
-------
Table VI-J-1. SUMMARY OF SPAWNING SALMON USE OF STREAMS IN THE
PORT ANGELES HARBOR AND ADJACENT WATERS
Source: Egan 1978; Egan 1979; Eg &n 1980
Length Salmon Historical Population (range )
Stream # Stream Name Years Inventoried (miles) Use Live Count Dead Count Max Total
0272 Elwha River 1952, 1961, 1963— 44.8 Chinook 0 - 58 0 - 37 95
1965, 1969, 1970, (spring &
1971, 1973 — 1975 fall)
Coho 0-233 0-7 239
Pink 0 - 1319 0 — 1517 2836
Chum 63 - 329 7 - 85 414
Sockeye 1 0 1
0265 Dry Creek 1975 4.8 Coho a 0 0
56 Tuwter Creek 1970, 1974, 197 5. lCoho
Chum 0 0 0
0249 Valley Creek 1974, 1975 4.9 Coho 0 0 0
Chum 0 0 0
0245 Peabody Creek 1975 4.8 Coho 0 0 0
Chum 0 0 0
0234 Ennis Creek 1970, 1974, 1975 8.7 Coho 0 - 8 0 - 2 10
Chum 0 0 0
0232 Lees Creek 1974, 1975 4.3 Coho 0 0 0
Chum 0 0 0
-------
Table VI-J-l page 2.
Length
Stream # Stream Name Years Inventoried (miles)
Salmon
Use
Historical
Population
(range)
Live
Count
Dead
Count
Max
Total
0185 Morse Creek 1944, 1955, 1967, 16.3 Chinook 2 1 3
1969, 1970, 1971, (fall)
1973 — 1976 Coho 0 - 276 0 — 5 281
Pink 0—143 0—3 146
Chum 0-1 0-1 2
0183 Bagley Creek 1974, 1975 7.05 Coho 0 0 0
Chum 0 0 0
0173 Seibert Creek 1952, 1970, 1972, 12.4 Coho 0 - 235 0 - 22 257
1974 — 1979 Chum 0 0 0
0160 McDonald Creek 1970, 1972, 13.6 Coho 0 - 100 0 - 64 164
1974 — 1979 chi 0 0 0
018 Dungeness 1944, 1952, 1961, Chinook 0 - 70 0 - 48 118
River 1964, 1969, 1971— (spring &
1979 fall)
Coho 0 — 1010 0 - 43 1053
Pink 0 — 9600 0 — 1709 11,309
Chum 0 — 189 0 — 61 250
Sockeye 1-3 0 3
* The years in which a stream was inventoried do not apply to each species listed under salmon use.
-------
Table Vi-J-2. NATURAL SALMON ESCAPEMENT ESTIMATES FOR PORT ANGELES, WASHINGTON
Source; Geist, personal communication of November 12, 1980;
Zillgis, personal communication of November 17, 1980
Elwha
Pink
Dungeness
Elwha
Morse
Coho
Siebert
McDonald
Dungeness
Year River
River
River
Creek
Creek
Creek
River
1961 8,000 70,000
1962
1963 40,000 400,000
1964
1965 15,000 75,000 130 100 120 80 710
1966 130 100 120 80 710
1967 10,000 95,000 130 100 120 80 710
1968 130 100 120 80 710
1969 1,500 14,400 50 40 50 30 280
1970 130 100 120 80 710
1971 4,000 46,000 130 100 120 80 710
1972 50 40 50 30 280
1973 9,600 47,000 130 100 120 80 710
1974 130 100 120 80 710
1975 1,500 24,500 50 40 50 30 280
1976 130 100 120 80 710
1977 5,000 35,500 130 100 120 80 710
1978 130 100 120 250 710
1979 7,100 50,000 130 100 120 150 710
Average!
year 10,170 85,740 114 88 90 86 624
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Table Vi-3-3. ARTIFICIAL ADULT SALMON ESCAPEMENTS FOR THE ELWHA 2 ND DUNGENESS HATCHERIES
Source: Rasch and Foster 1978; Fletcher et al. 1979; Egan 1980
Elwha Hatchery
Dungeness
Hatchery
Spring
Fall
Spring
Fall
Year
Chinook
Chinook
Coho
Chinook
Chinook
Coho
Pink(a)
1960
Not
Operative Until
1975
1,025
0
0
——
1961
472
0
0
0
1962
613
0
0
——
1963
417
0
0
0
1964
221
0
0
——
1965
398
0
5,146
0
1966
408
0
947
——
1967
285
0
1,294
0
1968
275
0
1,437
——
1969
90
0
4,541
0
1970
130
0
19,150
——
1971
541
95
16,534
0
1972
301
36
1,816
——
1973
90
59
1,010
0
1974
99
26
6,787
——
1975
77
95
20,934
16,667
1976
0
0
177
46
275
3,384
——
1977
503(b)
N/D
1,050
12
N/D
2,385
22,235
1978
379(b)
N/D
894
69
N/D
3,918
——
1979
469(b)
N/D
10,092
59
N/D
3,316
33,000
Average/
Year(c)
450(b)
N/D
803
281
98
6,167
23,967
N/D - no data in available publications
(a) - odd years only
(b) - Report does not separate spring and fall chinook; therefore this may represent both species.
(c) - Beginning with the first year that return runs occurred
-------
Table VI-j-4. ARTIFICIALLY REARED SALMON PLANTINGS FOR THE ELWHA
AND DUNGENESS HATCHERIES, 1977 AND 1978
Source: Foster et al. 1978; Fletcher et al. 1979
1977 Planting Year
TotalTi
of Fish
1978 Planting Year
Hatchery
Species
Days
Reared
Stream
Planted
Species
Days
Reared
Stream
Planted
Total #
of Fish
Elwha
Spring Chinook
469
Elwha
532,647
Fall Chinook
449
Elwha
97,063
Fall Chinook
187
Elwha
471,924
Coho
166
Elwha
75,335
Fall Chinook
453
Elwha
180,054
Coho
Coho
255
358
Elwha
E lwha
50,000
1,387,870
Coho
1
Dungeness
75,335
Dungeness
Spring Chinook
441
Dungeness
73,486
Spring Chinook
430
Dungeness
26,390
Coho
363
Morse
24,986
Spring Chinook
479
Dungeness
67,998
Coho
363
Siebert
15,600
Coho
348
Morse
25,300
Coho
363
McDonald
29,302
Coho
348
Siebert
14,996
Coho
370
Dungeness
87,178
Coho
348
McDonald
31,993
Coho
407
Dungeness
517,140
Coho
1
Dungeness
1,412,900
Coho
348
Dungeness
6,023
Coho
351
Dungeness
110,068
Coho
390
Dungeness
679,986
Pink
34
Dungeness
302,400
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Table VI-J-5. FRESHWATER SPORT SALMON CATCH FOR THE ELWHA AND DUNGENESS RIVERS
Source: Nye & Ward 1974; Nye et al. 1975; Nye et al. 1976; Nye
et al. 1977; Homes et a1 1978; Sekuli h, personal
communication of Nov ber 5, 1980
Chinook
Coho
Pink(l)
Jack(2)
Unidentified
Adult
All
E
Total
Species
D
E
D
E
D
E D
Year
E
D
E
D
1973
N/A
N/A
N/A
N/A
N/A
N/A
N/A
N/A
N/R N/R
14
23
1974
10
3
3
N/a
--
--
23
N/R
N/R N/R
36
3
1975
N/R
146
N/R
4,381
N/R
125
53
165
N/R 4
53
4,821
1976
N/R
14
14
1,301
——
—-
67
54
N/R 30
81
1,399
1977
N/a
N/R
51
254
N/R
N/R
22
29
N/a N/R
73
283
1978
3
60
88
764
——
—-
40
53
N/R 43
131
920
TOTAL
1973—78
13
223
156
6700
N/R
125
205
301
N/R 77
388
7449
E - Elwha River
D — Dungeness River
(1) - odd years only
(2) - Jack refers to any immature salmon species
N/A - not available in report
N/R - none reported
-------
Table VI-J-6. SUMMARIES OF STEELHEAD CATCH DATA IN PORT ANGELES, WASHINGTON
Source: WDG 1963 — 1979 (Angler Catch)
WDG 1975 - 1979 (Treaty Indian Catch)
Angler Catch
Summer Run Catch
Winter Run Catch
Elwha
Morse
Siebert McDonald Dungeness
Elwha Morse
Siebert McDonald Dungeness
Year
River Creek
Creek Creek
River
Year
River
Creek
Creek Creek
River
1962
4 55
N/P N/P
42
1961-62
646
136
N/P N/P
1615
1963
8 N/P
N/P N/P
18
1962-63
426
131
N/P N/P
1130
1964
13 13
N/P N/P
29
1963-64
1817
123
N/P N/P
3020
1965
34 2
N/P N/P
68
1964-65
779
106
N/P 23
1596
1966
67 N/P
N/P N/P
78
1965-66
991
93
N/P 25
1610
1967
41 2
N/P 2
67
1966—67
843
215
28 45
2284
1968
39 7
N/P N/P
80
1967-68
931
79
N/P 58
2071
1969
23 N/P
N/P N/P
50
1968-69
1554
95
N/P 32
1163
1970
58 N/P
N/P N/P
28
1969-70
803
50
N/P 23
817
1971
281 5
N/P 2
75
1970—71
1961
109
26 50
1713
1972
332 N/P
N/P N/P
99
1971-72
2091
86
N/P 47
2162
1973
145 N/P
N/P 2
23
1972—73
1178
38
2 4
687
1974
337 6
N/P N/P
77
1973-74
1270
86
12 4
647
1975
263 N/P
N/P N/P
67
1974-75
908
72
10 19
526
1976
341 N/P
N/P N/P
148
1975-76
345
10
N/P 9
359
1977
334 9
N/P N/P
163
1976-77
1119
19
N/P N/P
386
1978
1098 4
N/P N/P
179
1977-78
1978-79
1060
940
334
150
N/P 6
N/P N/P
1094
308
TREATY
INDIAN
CATCH
Year
Elwha River
Summer Run Catch
Dungeness River
Year
Elwha
River
Winter Run Catch
Dungeness River
1975
N/R
2
1975—76
697
585
1976
N/R
5
1976—77
774
226
1977
58
4
1977—78
998
N/R
1978
75
3
1978—79
1045
67
N/P — no angler punchcards returned
N/R - none reported
-------
APPENDIX IV-K
MARINE FISH ABUNDANCE AND BIONASS
-------
Table VI-K-1. MARINE SPECIES COMPOSITION OF BEACH SEINE HAULS
CONDUCTED IN THE PORT ANGELES AREA, 1961 — 1966
Source: Stein and Denison 1966
1961
1962
1964
1965
1966
Grand
Species 10/12
7/11—13
9/3
7/29—8/6
7/12
Total
Northern Anchovy 1 76 77
Cabezon 5 1 6
Pacific Dogfish 1 1
Starry Flounder 16 25 13 40 27 121
Flounder sp. (juvenile) 1 59 59
White spotted Greenhing 1 1
Greenling sp. (juvenile) 2 2
Crescent Gunnel 1 1
Saddleback Gunnel 1 1
Pacific Herring 799 42 533 1374
Lingcod 9 20 6 35
Shiner Perch 103 4 1 1 109
Striped Perch 1 1
Tubesnout Poach’r 19 19
Sturgeon Poacher 1 1
Snake Prickleback 203 41 171 61 476
Speckled Sanddab 2 2
Pacific Sandlance 1 2 3
Buffalo Sculpin 3 7 10
Pacific Staghorn Sculpin 3 25 15 6 49
Padded Sculpin 1 1
Sharpuose Sculpin 1 1
Tidepool Sculpin 5 5
Surf Smelt 2 4 3146 554 3706
English Sole 2 243 38 17 260
Sand Sole 76 1 77
Threespine Stickleback 1 8 1 10
Whiting (Wahleye Pol].ock) 1 1
Unidentified species 1 1
Total Species 16 15 10 13 9 31
Total Fish 959 567 124 4130 729 6529
A—190
-------
Table VI-K-2. AVERAGE NUMBER AND BIOMASS OF NEARSHORE FISH SPECIES COLLECTED
NEAR MORSE CREEK AND DUNGENESS SPIT, 1977 - 1978 (a)
Source: unpublished NOAA - MESA Data for Cross et al. 1978 report
Morse Creek 1977
BEACH SEINE(b)
May August September Deαember
Genera Species Common Name D B D B D B D B
9corpaenichthy8 lm3rmoratUa cabezon .54 6.03 No Sampling
This Month
Gobi eaox nueandrvoue northern clingfish —- - - -- -- 1.09 9.24 -- - -
‘Zatiohthys ateflatus starry flounder 114.1 1505 2.17 1176.9 .54 157.3
lpodichthjja fiavidua penpoint gunnel 2.2 35.7 -- --
Clupea harengue paliaei Pacific herring —- -- 1.09 2.23 -- —-
lniphietriohue rhodotez2ua redtai]. perch -- .54 44.24 .54 4.51
yrintogaeter aggregata shiner perch .54 2.88 -- -- 1.63 63.6
E nbiotoca lateraUa striped sea perch 1.63 1096.4 1.63 486.7 —— --
PcgUaeina barbata tubenose poacher -- —- 2.72 2.34 1.63 2.12
Ocelia verruooea warty poacher —- -- -- -- 1.63 4.95
Oncorhynchue kioutch coho salmon 4.89 117.7 4.89 67.07 -- --
Oncorhynchua t8hcA yt8cha chinook salmon 1.09 958.8 -- -- --
FIyd.roiague coliei ratfish -- -- -- -- .54 150
Citharichthye ati9maeua speckled sanddab -- -- .54 5.82 -- --
Animodytea hexapterua Pacific sand lance 3.80 6.74 -- -- -- --
Flypomeeua pretioaue surf smelt -- —— 9.78 285.3 10.3 204.2
Leptocottue annatua Pacific staghorn
aculpin .54 28.1 10.87 250.8 13.0 649.5
Eepeioe cirrhoaue silverspotted sculpin 3.26 30.71 2.7 9.9 11.96 88.7
Liparia fiorae tidepool. snailfish -— -- -- —- 1.09 3.48
Paettiohthye meianoetictue sand sole 2.7 21.7 31.5 133.2 76.]. 390.7
-------
Table VI-K-2. continued, page 2
Morse Creek 1977
BEACH SEINE (b)
May August September December
Genera Species Common Name D B D B D B D B
l4icrogadua proanmue Pacific tomcod -- -- 3.26 5.76 39.7 392.3 -— --
iulorhynchua favidua tube-snout -- -- 30.4 12.5 2.17 2.34 -- --
Morse Creek 1978
BEACH SEINE
May 1 ugust October
Genera Species Common Name D B D B D B
Cobiesox maeandricua northern clingfish
Platichthya ateUatua starry flounder
Hexagrcvnmus decagraminue kelp greenling
Pholia laeta crescent gunnel
Apodichthya fiavidue penpoint gunnel
Ciupea harengua pallaai Pacific herring
C ymatoga8ter aggregata shiner perch
E)nbiotoca lateralia striped sea perch
Pal Zaaina barbata tuhenose poacher
Ocoella verrucoea warty poacher
Theragra chaiogramna walleye pollock
Oncorhynohue keta chum salmon
citharichthya etigmaeue speckled sanddab
-- —-
- - - -
-- - -
-- --
- - --
- - - -
-- -—
-- - -
-- --
-- --
-- - -
7.0 142.9
- — - —
1.0 0.2
-- — -
-- --
1.0 3.5
4.0 25.1
9.5 12.0
- — —-
1.0 6.2
5.5 5.7
-- - -
- - - -
-- - -
-- --
- — --
1.0 111.5
4.5 125.4
0.5 1.6
-- - -
4.0 33.1
2.0 14.0
5.5 134.4
0.5 0.6
0.5 1.5
1.0 4.05
-- - -
4.0 39.2
-------
Table VI-K-2. continued, page 3
Morse Creek 1978
BEACH SEINE
May August October
Genera Species Common Name D B D B D B
Anvnodyteo hexapterue Pacific sand lance
Synchirue gilli Manacled sculpin
Leptocottua armatus Pac. staghorn sculpin
Artediuo feneotralie padded sculpin
Blepaioa cirrhoeuo silverspotted sculpin
!iypomesuB pret4 oaua surf smelt
Paraphryo vetulue English sole
&ticrogadue proxirnue Pacific tomcod
Aulorhynchuo favi duo tube-snout
—- ——
— - -—
0.5 58.9
0.5 0.7
——- -—
35.0 20.7
8.5 15.5
-- - -
-- --
2.0 3.9
0.5 0.4
2.5 155.0
—- -—
14.5 46.8
1.0 1.4
-- --
13.0 52.5
0.5 1.0
—— —-
-- --
5.5 314.2
0.5 4.3
1.0 12.6
183.5 1740.9
3.5 8.1
-— --
0.51 2.8
Morse Creek 1977
TOWNET (b)
May August October December
Genera Species Common Name D* 8* D* B* D* B* D* B
Engraulie mordax northern anchovy
Squalie acanthiaa spiny dogfish
lpodichthyo flavidue penpoint gunnel
Clupea harengue pallasi Pacific herring
Oncorhynchua keta chum salmon
lnvnodytee hexapterue Pacific sand lance
-- --
-- —-
-- --
8831 338
-- --
539.1 29.7
-- --
2.17 1010
-- --
131,590 305,180(c)
1.09 29.24
115.7 245.3
.54 .05
-- --
1.09 .9
25.5 85.2
-- --
3.8 5.33
-- --
-— --
-- --
.54 4.78
-- --
-- —-
-------
Table VI-K-2 . continued, page 4
Morse Creek 1977
TOWNET (b)
May August October December
Genera Species Common Name B* D* B* B* D* B*
E ’nophry8 biaon buffalo sculpin -- -- .54 .49
Radul.inus boleoide8 darter sculpin - — -- 23.4 6.96 -- -- -- --
Synchirua gilli manacled sculpin .54 .8 2.18 .54 .54 .6
Leptocottua armatuB Pac. staghorn sculpii -- -- .54 77.2
PBychrolute8 paradoxua tadpole sculpin 3.26 .71 -- --
Spirinahue thaleichthya longfin smelt -- -- .54 .60
FIypomc8u8 pretiO8u8 surf smelt 1.41 --
Liparis florae tidepool snailfish -- -- .54 8.26 --
( Iicrogadua proximue Pacific tomcod .54 1.20 .54 1.47
Aulorhynchu8 favidus tube—snout -- -- -- 1.6 2.99
Cottidea .5 .33 -- --
Gadidae 2.2 1.6
Pholidae \.09 .1
Pleuronectidae 1.3 .3 - - --
Teleostei L2 .16 .54 0
-------
Table VI-K-2. continued, p e 5
Morse Creek 1978 - 1979
TOWNET
May 1978 Au ust 1978 October 1978 January 1979
Genera Species Common Name D D B* D B*
Engrx ulia mordax northern anchovy
PholiB iaeta crescent gunnel
Ciupea harengus pallaai Pacific herring
Oncorhynchue keta chum salmon
Ain’nodl/teB hexapteru8 Pacific sand lance
Synahirue gilU manacled sculpin
Leptocottue armatue Pac. staghorn sculpin
BlepBioa cirrhoaua silverspotted sculpin
Paychrolutee paradoxue tadpole sculpin
Hypomeeue pretioaUa surf smelt
Aulorhynchue favi due tube-snout
Agonidea
Gadidae
-- --
3.0 2.8
518 14.7
-- --
9.0 3.1
-- --
1.0 73.9
8.0 1.0
161.0 36.3
-- ——
2.. 0 8.2
2.0 0.1
1.0 0.9
1.5 0.5
-- --
35.5 132.5
0.5 22.0
—- --
1.5 0.8
-- --
-- --
-- --
-- --
-- --
-- --
1.5 1.0
-- --
—- --
-- --
-- --
0.5 2.6
-- --
-- --
—- -—
-- --
0.5 8.2
-- --
- - --
—- -—
-- --
- - --
-- --
-- --
-- --
-- --
-- --
-- --
-- --
-— --
- - --
-- - -
-- ——
Morse Creek 1977
V INTERTIDAL
February April May July(d) August November(d) December
3 hauls 4 hauls 4 hauls 7 hauls 6 hauls 6 hauls 1 haul
6 hauls 3 hauls 5 hauls
Genera Species/Common Name D**/B** D**/B** D**/B** D**/B** D**/B** D**/B**
Gobieaox meo.ndricue/
northern clingfish
Anopl.arc hue purpureacene/
high cockscomb
.78/3.77
.77/.84
1.1/5.01
1.43/3.81
.88/5.02
5.36/17.01
.61/3.37
2.09/5.1(e)
.22/1.5
5.0/25.8
.33/2.6(d)
.33/1.48
1.1/.99
1.5/5.1
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Table VI-K-2. continued, page 6
Morse Creek 1977
INTERTIDAL
February April May July(d) August November(d) December
3 hauls 4 hauls 4 hauls 7 hauls 6 hauls 6 hauls 1 haul
6 hauls 3 hauls 5 hauls
Genera Species/Common Name D**/B** D**/B** D**/B** D**/B** D**/B** D**/B**
Pholia l.aeta/
crescent gunnel - — I—— 1.43/2.48 .80/1.45 .66/1.6(e) .33/2.1 .44/0.9(e) —-1-—
Apodiothya flavidue
penpoint gunnel ——1—— .55/1.35 —-I—- -—I—- —-I—— 1.43/4.64 —-I-—
Xiphia tar atropurpureua/
black prickleback .--/—— ——1—- —-1—- .99/1.5(e) -—1—— .44/2.08 —-I--
xiphiater mucoaua/ /
rock prickleback —— I—— ——1—- —-I—- .77/8.5(e) .55/8.9 1.76/9.9(e) .22/1.34
Ciinocottua embryum/
calico sculpin —- 1-- —-/—- .33/0.14 Ce) -—I—- -—I-- --I-— --I-—
OZigocottua anyderi/
fluffy sculpin —-/-— —-I— - —-I —- -—I—- 0.33/0.03 -—1-- —-1-—
Clinocottua globiaepa/
mosshead sculpin ——/—— .33/.03 .33/.51 .11/.01(e) .33/.19 ——1—— 1J1/8.03
Aece lichthy8 rhodoraa/
rosylip sculpin ——/—— 1.98/3.19 .88/4.13 .39/2.13 .22/.93 .33/2.8(e) 1.1/10.89
Oligocottua rinienaia/
saddleback sculpin —-1-- —-1—- —-/—- -—I—- --I-— .33/.49(e) 1.1/1.9
Ciinocottua acuttcepa/
• 1 sharpnose sculpin ——/-— .33/.14 .47/.34 l.29/.37 -—I-— .33/.19 Ce) .8/1.05
Artediua Zateralis/
smoothhead sculpin -- I-- —-I -- --1-- -- I-- -- I-- .22/.46 Ce) .25/1.1
Oiigocottua nuculoaua/
tidepool sculpin 1.1/.44 2.75/2.2 2.58/3.57 .611.93 .55/.99 .77/.77(e) 8.8/42.1
-------
Table VI-K-2. continued, page 7
Morse Creek 1977
I-
INTERTIDAL
February April May July (d) August November Cd) December
3 hauls 4 hauls 4 hauls 7 hauls 6 hauls 6 hauls 1 haul
6 hauls 3 hauls 5 hauls
Genera Species/Common Name D**/B** D**/B** D*t/B** D**/B** D**/B** D**/B**
iparia rutteril
ringtail snailfish
iparia fiorae/
tidepool snailfish
-—/-—
.33/1.7
-—/—-
——/——
——/-—
.33/3.19(e
-—/---
.11/.07(e)
--/-—
.33/.44
---/--
——1——
.22/.36
.33/.14
Morse Creek 1978
INTERTIDAL
January February March April June (d)
4 hauls 4 hauls 5 hauls 5 hauls 6 hauls
ihaul
Genera Species Common Name D** B** D** B** 1** B** D** B** D** B**
QQb eqox r eandricu northern clingfish
Anoplarchue purpur... high cockscomb
eacena
Phol4a Zaeta crescent gunnel
Apodicthy8 fjavidua penpoint gunnel
Xiphiatez’ atropur— black prickleback
pureua
Dhytichthye chiraa ribbon prickleback
Xiphiater niucoaua rock prickleback
Clinocottue embryum calico sculpin
2.5 2.5
2.5 1.4
—— ——
0.3 0.2
-— -—
- — -
-— --
-— -—
—— ——
1.8 1.6
0.3 0.2
0.5 1.9
5.5 11.3
--
0.2 0.2
—- --
0.4 0.8
0.8 0.6
-— -—
0.2 0.6
-— -—
-— --
0.2 0.3
-— -—
2.0 5.9
2.6 3.6
2.2 3.3
0.2 1.3
0.2 0.1

0.2 3.6
-- —-
2.7 11.6
2.5 2.5
0,2 0.2
-— --
-- —-
3.0 11,1
1.2 8.7
13.0 1.8
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Table VI—K-2. continued 1 page 8
Morse Creek 1978
INTERTIDAL
January February March April June(d) -
4 hauls 4 hauls S hauls 5 hauls 6 hauls
1 haul
Genera Species Common Name D** B D** B** D** B** D** B** D** B**
Clinocottue globicepa mosshead eculpin
Aaoeliahthjje rhodoraa rosylip sculpin
OUgocottue r1 menaia saddleback sculpin
Clinocottus acuticepa sharpnose sculpin
Artediue l .ateralia smoothhead sculpin
Oligocottue nucuioeua tidepool sculpin
Liparia c jclopsue ribbonhead snailfish
Liparia utteri ringtail snailfish
Liparie florae tidepool snailfish
—- ——
0.3 0.3
0.3 0.1
0.3 0.2
1.3 6.1
0.5 0.3
-- --
0.3 0.5
—— --
—- ——
0.2 3.1
—— --
0.4 0.1
—— --
6.0 3.5
0.2 1.3
0.2 0.5
—— ——
—- —-
0.8 3.0
0.2 0.04
—- —-
-- --
12.6 8.9
-- - -
—- —-
0.4 5,8
--
1.6 6.1
—— — —
-- --
0.6 2.8
4.0 3.5
-- --
—- -—
—- --
1.0 0.5
0.2 6.8
- - --
—- ——
-- -—
2.3 2.6
-- --
—- -—
— - --
Dungeness Spit 1977
BEACH SEINE
May August September December
Genera Species Common Name D B D B D B D B
Gobieoox ,m2eandricua northern clingfish
Platichthya atell.atua starry flounder
Pholia Zaeta crescent gunnel
Ap dichthya flavidue penpoint gunnel
Pholia ornata saddleback gunnel
— — —-
—— —-
-- —-
.54 184.8
-— --
1.63 8.32
2.2 95.8
31 43.8
10.9 269.2
13.0 183.3
-— -—
-- -—
-— --
-— ——
-— -—
.54 391.3
-— —-
-— — -
-— --
-— —-
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Table VI-K-2. continued, page 9
Dungeness Spit 1977
BEACH SEINE
May August September December
Genera Species Common Name D B D B D B D B
Clupea harengus paflaei Pacific herring
Cyn itogaeter aggregata shiner perch
PaUa8ina barbata tubenose poacher
Occe i la uerrucoaa warty poacher
Lwnpenua eagitta snake prickleback
Arivnodytea hexapterue Pacific sand lance
Enophrya bison buffalo sculpin
Leptocottue ar’ natuB Pac. staghorn sculpin
Artedius feneatralie padded sculpin
Liparia rutteri ringtail snailfish
Pleuronichthya coenoaua c-O sole
Parophrya vetulue English sole
Paettiohthya melanoatictua sand sole
Miarogadue proxiinue Pacific tomcod
-— ——
1 1 6.1
-- --
-- --
2.1 53.9
—— —-
-— —-
1.1 39.7
.54 1.58
—— ——
-— --
—— ——
2.7 43.7
- — -—
.54 .54
-- --
.54 .54
12 15.4
-— -—
4.4 11.9
.54 8.2
.54 8.2
.54 2.6
—— ——
1.1 .4
14.7 118.9
31.5 123.6
102.7 458.7
-- --
-- --
-— --
-- --
-— —-
-— —-
—— — -
-— —-
—— —-
-- --
—— ——
—— ——
-— --
.54 1.74
-- --
-- --
-- - -
-- --
-— —-
3.8 14.1
-— —-
4.89 12.0
4.4 11.9
-- --
1.1 2.8
2.7 7.1
-- --
Dungeness Spit 1978 — 1979
BEACH SEINE
May 78 Aug 78 Oct 78 Jan 79
Genera Species Common Name D B D B D B D B
Engraulia nzordax northern anchovy -— -- -- —- 14.0 4.4 -- --
Gobieaox niieandricua northern clingfish 0.5 0.4 —- -- -- -- -- --
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Table VI-K-2. continued, page 10
Dungeness Spit 1978 — 1979
BEACH SEINE
May 78 Aug 78 Oct 78 Jan 79
Genera Species Common Name D B D B D B D B
Piatichthy8 eteUatu8 starry flounder - — -- 0.5 48.5
He grammaa decagranraua kelp greenling -- -- 9.0 173.6 0.5 1.3
Clupea harengue pail.aai Pacific herring 3.5 5.1 —— -- — - --
Cymatogaeter aggregata shiner perch -— -- 42.0 297.0
E ’nbiotoaa 1.ateralio striped perch 3.0 1687.8 -- --
Syngnathu8 grieeolineatue bay pipe fish -— —— 2.0 10.9
Pallaeina barbata tubenose poacher -- —- 1.0 1.2 -- -- -- --
Oocel.Za vex*rucoaa warty poacher 0.5 0.0 2.0 3.8 3.0 4.1 0.5 0.7
Citharichthye aordidua Pacific sanddab —- —- 0.5 1.5 -- - - - - --
Cithar?chthya atigiwieue speckled sanddab 6.0 48.4 2.0 20.5 3.5 32.6
Enophrya biaon buffalo sculpin —— —- —- —- -— -— 19.5 103.8
LeptocottuB arnntue Pacific staghorn 2.0 139.7 15.0 416.5 5.0 211.8 9.5 462.5
sculpin
Artedizse fene8traUa padded sculpin — - —— -- -- 1.0 15.9 - - --
Blepaioe cirrhoaua si1vers otted —— —— 1.5 4.4 1.0 3.6 0.5 3.0
sculpin
Hypomeaus pretioaua surf smelt 62.5 10.4 -— -- -— -— —- -—
Liparie rutterz ringtail snailfish 0.5 1.8 —— —— 4.0 29.8 -—
Paettiohthya metanoetictue sand sole 35.0 150.3 95.0 1154.6 110.0 903.4 17.5 120.2
Caateroateua aculeatua threespine stickle- —- —— -— -- -— -— 2.0 10.9
back
Miorogadua proximua Pacific tomcod 5.0 53.3 -- —— 19.5 186.5
Aulorhynchua favidue tube .usnout -- -- 1.0 6.9 367.0 177.9
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Table VI—K-2. continued, page 11
Dungeness Spit 1977
TOWNET
May August October December
Genera Species Common Name D* B* D* B* D* B* D* B*
EngraUil.a mordax northern anchovy -- -- 16.9 2.4 1.63 .6
Squalia acanthias spiny dogfish -- -- 6.5 3627.7 -- -- - - --
Pholia lasta crescent gunnel 1.6 1.0 -— —- -— -— — — --
Clupea harengue paflasi Pacific herring 4579.4 179.1 134.2 294.6 85.9 412 3.3 16.5
Cynv2togaater aggregata shiner perch -- —- -— —- .54 4.0 -- --
Syn9nathus griaeolineatue bay pipe fish -- -- .54 .3
Oncorhynchua tahawijtaoha chinook salmon - - -- 2 • 2 36.3 -- -- --
Animodyte8 heaupterua Pacific sand lance 449.5 41.7 6.5 9.1 6.5 10.4 .54 1.52
Enophrya bison buffalo sculpin .54 .9 -- -- -- —- --
Rharnphocottua richardaoni grunt sculpin -- -- .54 .71
Gzlbertidia aigalutea soft sculpin —— .54 1.1
Paychrolutes paradoxua tadpole sculpin 3.3 .6 -- --
Spirinchua thaieichthya longfin smelt -— .54 .1 -- --
Hypomeaue pretiosue surf smelt -— —- -— -— 1.6 17.5
Liparia pulohellue showy snailfish -— —- —— .54 .54 —- --
Parophrya vetulue English sole 3.3 1.1 .54 1.5 —— ——
?dLor’ogadus proximue Pacific tomcod -- —- 4.9 6.9 2.7 15.9
a4ul.orhynohue favidue tube-snout 1.6 3.0
-------
Table VI—K—2. continued, page 12
Dunqeness Spit 1978 - 1979
-S
TOWNET
May 78 Aug 78 Oct 78 Jan 79
Genera Species Common Name D* B* D* B* D* B* D* B*
Eflgrauli8 rnordax northern anchovy
PhoUa iaeta crescent gunnel
CZupea harengua palla8i Pacific herring
Anrmodyte8 hezapterua Pacific sand lance
Enophrya biBon buffalo sculpin
Jlypomesua preti..oaua surf smelt
Parophrye vetul u8 English sole
Gaateroateuo acuieatua threespine stickle-
back
- - --
1.0 0.6
3895.0 89.2
3.5 5.7
0.5 1.4
52.5 18.5
—- --
—— --
201.5 35.6
- - --
—— -—
2.5 3.9
-- --
—— -—
0.5 1.0
0.5 0.2
1.5 0.6
-- --
19.0 105.6
-- --
-- --
-— -—
-- --
0.5 0.4
No Sampling
-- --
-— --
-- --
-- --
-— --
-- --
-— —-
(a) — Occurrence data collected in 1976 is very similar to 1977 — 1978 data and is not included
in this report.
(b) — All beach seines and townets are the average of two samplings performed at each station,
unless indicated differently.
Cc) - total number of fish and total biomass
Cd) - average determined from two separate sampling dates during the month
(e) - Species occurs only during 1 sampling date.
Density (D) and Biomass (B) :
D = mean # fish/l000 m 2 ; B = mean biomass/1000 m 2
D* = mean fish/l1,000 m 3 ; B* = mean biomass/1],000 m 3
D** = mean # fish/# of hauls; B** = mean biomass/# of hauls
-------
APPENDIX Vu-A
SEASONAL FOODWEBS AT MORSE CREEK
AND DUNGENESS SPIT
Source: Simenstad (unpublished)
-------
Figure Vu-A—i.
PORT ANGELES REGION
SAND - COBBLE
(MORSE Ct EK)
SPRING
SHALLOW SUBLITTORAL FOOD WEB
A—2 04
-------
PORT ANGELES REGION
Figure VII-A-2.
SAND - COBBLE
(MORSE CREEK)
SUMMER
SHALLOW SUBLITTORAL FOOD WEB
HARBOR
SEAL
A— 205
-------
PORT ANGELES REGIO 1
Figure VII—A-3.
SAND - COBBLE
(MORSE CREEK)
FALL
SHALLOW SUB LITTQRAL FOOD WEB
A—206
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PORT ANGELES REGION
Figure VII-A-4.
SAND - COBBLE
(MORSE CREEK)
WINTER
SHALLOW SUBLITTORAL FOOD WEB
A—207
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PORT ANGELES REGION
Figure VII—A—5.
SAND - GRAVEL
(DLThIGENESS SPIT)
SPRING
SHALLOW SUBLITTORAL FOOD WEB
A— 208
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PORT ANGELES REGION
Figure VII—A—6.
SMID - GRAVEL
(DUNGENESS SPIT)
SUIG2ER
SHALLOW SUBLITTORAL FOOD WEB
A—2 09
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Figure VII-A—7.
PORT ANGELES REGION
SAND - GRAVEL
(DUNGENESS SPIT)
FALL
SHALLOW SUBLITTORAL FOOD WEB
A—210
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PORT ANGELES REGION
Figure VII-A—8.
SAND - GRAVEL
(DUNGENESS SPIT)
WINTER
SHALLOW SUBLITTORAL FOOD WEB
COMMON MEBGANSER]
A— 211
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Figure VII-A-9
PORT ANGELES REGION
SPRING
NERITIC FOOD WEB
A— 212
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PORT ANGELES REGION
Figure VII—A—1O.
SU 4ER
NERITIC FOOD WEB
IORCAI
A—213
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Figure V u—A— h.
PORT ANGELES REGION
FALL
NER.ITIC FOOD WEB
M42WROMOUS
RAZNBOW
TROUT
(Adult
Non-feeding )
A—214
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Figure VII-A-12.
PORT ANGELES REGION
WIt ITER
NERITIC FOOD WEB
F GFJ 1
I WI ALE 1
A—2 15
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APPENDIX VIII-A
CALCULATION OF BULK RESIDENCE TIME FROM SSL DATA
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APPENDIX VIII-A
CALCULATION OF BULK RESIDENCE TIME FROM SSL DATA
The bulk residence period CT) may be expressed as
T= ZSSL
R (1)
where R. is the input rate of SSL to the Harbor and SSL is the
total amount of SSL in the Harbor. The application of eq. Cl) to
the Harbor is not straightforward for two reasons. First, the
SSL input R is uncertain because the ITT Rayonier mill is loca-
ted at the Harbor mouth. This mill discharges approximately 0.88
of the total SSL but we are uncertain what fraction enters the
Harbor. Therefore we restricted our examination to intervals when
ITT Rayonier input was negligible. Second, the SSL undergoes
significant natural decomposition during periods of several days.
In eq. (1) the total SSL has resided in the Harbor for period T
and thus has undergone some decay. To apply eq. (1) it is
necessary to derive an expression for SSL decay.
The decay of SSL has been measured by West].ey (1960) in a small
lagoon. He showed that initial SSL concentrations decreased ex-
ponentially where the decay rate increased with increasing temp-
erature. One of his experiments was performed at a mean tempera-
ture of ll.7 0 C. Since the surface water temperatures in the Har-
bor are generally less than this value his data at ll.7 0 C may
provide an upper limit to the SSL decay in the Harbor assuming
that the results in the lagoon may be applied to the present open
system.
Inspection of Westley’s (1960) data shows that the decay may be
expressed as
SSL It) = SSL (0) eth’T (2)
where SSL It) has been expressed as a function of time Ct), and
P is the time constant (i.e. the time required to reach a concen-
tration of approximately 0.37 of the initial concentration).
A—217
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Eq. (1) may be approximated by a series expansion, or
SSL Ct) = SSL (0) Li — 2 —
We can simplify eq. (3) by considering the decay time T and an
upper limit for the residence period T obtained when the SSL
discharge stopped for a time.
On November 12, 1964 SSL discharge into the Harbor abruptly
ceased. During the following two weeks SSL concentrations were
measured at several locations in the Harbor. After four days
the SSL concentrations had decreased to small values at all loca-
tions (Figure VIII-A-l). These data indicate that the mean
residence period is less than four days. Since T is significantly
shorter than T = 12 days from Westley’s (1960) data, we can
approximate eq. (3) using only the linear terms, or
SSL CT) = SSL (0) — (4)
substituting eq. (4) into eq. (1) and solving the resulting
quadratic equation we obtain
T = . [ 1 ± (1 — (T)) (5)
Eq. (5) may be evaluated for the Harbor during reasonably long
intervals when only the Fibreboard plant was discharging SSL.
A— 218
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250
200 -
EI5Q-
a 1
-J
100-
C’,
50 -
0— i i i i—i ‘
12 $6 20 24 30
DATE
Figure VIII-A-1. CONCENTRATION OF SPENT SULFITE LIQUOR AT THE
HEAD OF PORT ANGELES HARBOR AFTER ABRUPT INCREASE
IN EFFLUENT DISCHARGE ON NOVEMBER 12, 1964
Source: Ebbesmeyer et al. 1979
A-219
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APPENDIX VIII—B
LETTER TO DOE FROM PROF. CLIFFORD A. BARNES ON DOWNWARD TRANSPORT
PROCESSED IN THE PUGET SOUND SYSTEM
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APPENDIX VIII-B
LETTER TO DOE FROM PROF. CLIFFORD A. BARNES ON DOWNWARD TRANSPORT
PROCESSED IN THE PUGET SOUND SYSTEM
“Following the 1971 spill of Number 2 diesel oil at the Texaco
refinery dock near Anacortes, University of Washington personnel
operating a laboratory on Kiket Island noted diesel oil odor in
seawater pumped into the Laboratory from a subsurface intake.
No oil slick was seen on the surface of the bay. The probable
sequence is that some of the oil ebbing from Guemes Channel
south through Rosario Strait was carried by the ensuing flood
through highly turbulent Deception Pass. It then carried in the
more saline influx under an interior low salinity surface layer
without rising through it. Due to the net outflow through Decep-
tion Pass and the rapid flushing northward from the Skagit Delta
most of the oil carried inward on flood probably was carried out
on the next ebb. A spill of comparable size in Rosario Strait
closer to Deception Pass at certain current phases would have
resulted in greater inward transport through Deception Pass, but
it is likely that any significant amount would reach Puget Sound
proper through this route. The Admiralty Inlet-Main Puget Sound
Basin situation is much more vulnerable owing to close proximity
of the very deep and slow flushing basin just inside the sill
combined with the net flood at depth. Likewise deep waters of
the slow flushing Strait of Georgia are directly vulnerable to
spills that might occur in either the Haro Strait-Boundary Pass
or Rosario Strait approaches.”
A— 221
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