Oceanographic and
Related
Water Quality
Studies
•2
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Sour rn Alaska
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OCEANOGRAPHIC AND RELATED WATER QUALITY STUDIES
IN SOUTHEASTERN ALASKA, AUGUST 1965
U. S. Department of the Interior
Federal Water Pollution Control Administration
Northwest Region
Portland, Oregon
July 1966
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INTRODUCTION
Upon request of the Alaska Department of Health and Welfare,
related oceanographic and water quality studies were conducted at
four locations in Southeastern Alaska. These studies, preliminary
in nature, were conducted in: Gastineau Channel, adjacent to the
cities of Juneau and Douglas; Fritz Cove-Auke Bay, near Juneau;
Silver Bay, near Sitka; and Ward Cove, near Ketchikan (see
Frontispiece).
The urgent need for a sewage and sewage treatment system to
serve the cities of Juneau and Douglas, Alaska, and surrounding
Borough necessitated the request for an oceanographic and related
water quality survey of Gastineau Channel. Gastineau Channel
borders Juneau, Douglas, and the expanding suburban areas, and now
receives untreated and partially treated wastes from the tributary
population. The Division of Health, Alaska Department of Health
and Welfare, has previously recommended early development of a
master sewage plan for the area, but lack of funds has precluded
initiation of such a project. A preliminary study of the currents
and water quality in this area was needed to provide information on
the chemical and bacteriological quality of the waters in the
immediate area and the Channel's ability to disperse the wastes
discharged into it.
Fritz Cove is under consideration as the site for a pulp mill
proposed in conjunction with plans to harvest nearly 9 billion board
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feet of timber from the surrounding Tongass National Forest. The Fritz
Cove and adjacent Auke Bay area also is very important in its natural
state because of its utilization in research programs of the U. S.
Bureau of Commercial Fisheries laboratory on Auke Bay and because of
its potential development as a residential and recreation area for the
expanding city of Juneau. A preliminary study of Fritz Cove was needed
to describe water circulation characteristics which would be pertinent
to consideration of the Cove as a suitable area for discharge of pulp
mill wastes.
The surveys of Silver Bay and Ward Cove were conducted to
describe the distribution of wastes from pulp mill operations at these
two locations and to determine the effect of these wastes on water
quality. We are fortunate in this case to have comprehensive water
quality information for both areas prior to commencement of pulping
and discharge of wastes; studies of Silver Bay and Ward Cove were
conducted by the Division of Public Health, Alaska Department of Health
and Welfare prior to pulp mill construction in each area. Data from
these studies were available for our evaluation of water quality
changes due to pulping operations.
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TABLE OF CONTENTS
CHAPTER 1. GASTINEAU CHANNEL STUDY
Study Objectives 1
Area Description .... 2
Studies 3
Methods --_ ______ 4
Results 7
Water Circulation 7
Tides and Tidal Currents 7
Salinity-Freshwater Relationships 9
Net Circulation 10
Water Quality 12
Dissolved Oxygen 12
pH — 13
Bacterial Quality 14
Conclusions and Recommendations 16
Conclusions 16
Recommendations 17
Outfall Location 17
Follow-up Studies 18
CHAPTER 2. FRITZ COVE STUDY
Study Objectives 19
Area Description 20
Studies 21
Methods 22
Results 23
Water Circulation 23
Tides and Tidal Currents 23
Salinity-Freshwater Relationships 25
Net Circulation 25
Water Quality 27
Conclusions and Recommendations 28
Conclusions 28
Recommendations -_-- 31
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CHAPTER 3. SILVER BAY STUDY
Study Objectives 33
Background 34
Studies 36
Methods 36
Results 38
Physical Conditions During Sampling Period 38
Waste Distribution 39
Water Quality 40
Dissolved Oxygen 40
pH 41
Secchi-disc 41
Discussion 42
Waste Distribution 42
Water Quality > 43
Dissolved Oxygen 43
pH — -- - 46
CHAPTER 4. WARD COVE STUDY
Study Objectives 48
Background 49
Description of the Waste Source — 50
Studies 53
Methods 53
Results 54
Physical Conditions During Sampling Period 54
Waste Distribution 55
Water Quality 55
Dissolved Oxygen 55
pH 56
Secchi-disc 57
Discussion 58
Waste Distribution 58
Water Quality 59
Dissolved Oxygen 59
pH - - - 61
LITERATURE CITED --- 62
APPENDIX 63
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CHAPTER 1
GASTINEAU CHANNEL
STUDY
August 17-20, 1965
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STUDY OBJECTIVES
Objectives of the Gastineau Channel Study were to:
1. Describe water circulation and water quality in
Gastineau Channel with a view toward locating a
proposed sewage treatment plant outfall.
2. Recommend an outfall site based on studies conducted,
3. Describe bacteriological conditions resulting from
present waste disposal practices.
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AREA DESCRIPTION
Vc
Gastineau Channel (Figure 1-1) is a long, narrow tidal inlet
connected to Stephens Passage at its seaward end and terminating
in an extensive tide-flat area. A small navigation channel, passable
only at high tide, connects the inner tide flats of Gastineau Channel
with those of Fritz Cove. Depths in Gastineau Channel vary from 40
fathoms at its entrance to the exposed tide flats at its terminal
end.
There are no major freshwater tributaries to Gastineau Channel.
.j
Runoff is primarily from local drainage adjacent to the channel. From
surface water records (1), peak discharges occur in late summer from
snowmelt and, on a mean-monthly basis, are estimated to collectively
average 1,000-1,400 cu. ft. per second.
The Juneau-Douglas area of Gastineau Channel (Figure 1-2) is
irregular in shape with depths varying from 20 fathoms in the expanded
channel section to 11 fathoms through the channel constriction under
the Juneau-Douglas Island bridge.
^Figures follow page 18
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STUDIES
Investigations were focused in Gastineau Channel near the
Juneau-Douglas Island highway bridge (Figure 1-2), both because
of apparent increased turbulence through the channel constriction
at this point, which could enhance initial waste dispersion, and
because of its central location in relation to the Greater Juneau-
Douglas area.
Two sampling stations, one located on either side of the bridge
(Figure 1-2), were occupied over separate 12-hour tidal cycles for
the purpose of describing variations in water characteristics and
current, and the mixing effect of the channel constriction under the
bridge. Station 1 was occupied on August 17 and Station 2 was
occupied on August 18, 1965. Measurements of water temperature,
salinity, dissolved oxygen (DO) content, and pH were made at hourly
intervals at the surface, 2, 5, and 10 meter depths at Station 1,
and the surface, 2, 5, 10, 20, and 30 meter depths at Station 2.
Current speed and direction were measured at approximately half-
hourly intervals at the surface and 8 meter depth at Station 1, and
at the surface and 16 meter depth at Station 2.
Longitudinal distributions of salinity, temperature, dissolved
oxygen, and pH at the 2 meter depth in Gastineau Channel were
continuously monitored along mid-channel between Thane and Juneau
boat basin (Figure 1-1) during a low water slack on August 19.
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Salinity and temperature were measured at the surface, 2, 5, 10,
20, and 30 meter depths at six stations in Gastineau Channel
(Figure 1-1) during a high water slack on August 20.
Current float studies were made on August 18, 19, and 20 through-
out th'e Juneau-Douglas area of Gastineau Channel for the purpose of
describing local and general water circulation patterns. Floats were
released at various locations and depths during both flood and ebb
tides.
Rhodamine B dye, a fluorescent tracer material, was released at
the water surface under the bridge during a flood tide on August 17
and during an ebb tide on August 20. Purpose of the dye releases
was to provide information on local circulation which would affect
immediate waste dispersal from a. source located near the bridge.
Bacteriological samples were collected on August 23 at the
twenty-five stations shown on Figure 1-3. These samples, collected
at low water slack, reflect the bacteriological quality of the
waters adjacent to the cities of Juneau and Douglas. These waters
presently are receiving raw sewage from numerous outfalls located
along the waterfront (Figure 1-4).
Reduced data from all studies will be presented and discussed
in this report. All raw data is on file at the Federal Water
Pollution Control Administration office in Portland, Oregon.
METHODS
Water sampling and current measurements at Stations 1 and 2,
and the continuous monitoring of DO, pH, and Rhodamine dye were
conducted from the 45-foot oceanographic research vessel,
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HAROLD W. STREETER. A high-speed 14-foot outboard boat was used to
conduct the current float studies, aid in the dye studies, and conduct
the six-station high water slack salinity-temperature traverse along
Gastineau Channel.
Individual water samples were collected using standard 1.25-liter
teflon-coated Nansen bottles. A submersible pump arrangement was used
to provide for continuous underway monitoring of DO, pH, and Rhodamine
dye.
Salinity, in parts per thousand, and temperature, in degrees
Centrigrade, were measured in situ using an Industrial Instruments,
Inc. model RS-5 inductive salinometer. Occasional check measurements
of salinity were made using a precision hydrometer and standard
oceanographic density tables.
Dissolved oxygen content was measured using a Beckman model 777
polarographic DO analyzer calibrated in percent saturation.
pH was measured using a Beckman model Zeromatic pH meter.
Fluorescent measurements of Rhodamine dye were made with a Turner
model 111 fluorometer equipped for both flow-through and discrete
sample monitoring.
Current measurements at Stations 1 and 2 were obtained using
two Hydro-Products Savonius-rotor current meters. Deck read-out units
indicated current speed in knots and current direction in degrees
magnetic. Float studies were conducted using conventional crossed-vane
current drogues suspended from small marker buoys. Buoy locations
were determined using a sextant and three-arm protractor.
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The bacteriological samples collected were analyzed by both the
membrane filter technique for total count and the most probable number
coliform test as described in Standard Methods(2). The MPN determina-
tions were conducted by the Alaska Department of Health at their
laboratory, while the membrane filter analyses were conducted in the
laboratory of the survey vessel HAROLD W. STREETER.
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RESULTS
WATER CIRCULATION
Tides and Tidal Currents. Tides throughout the Alaska area are
of the mixed semi-diurnal type characterized by two unequal high and
two unequal low waters per tidal day (about 25 hours). Daily
predictions of tides and currents in Gastineau Channel at Juneau are
listed in the tide and current tables (3, 4) of the U. S. Coast and
Geodetic Survey. Mean values listed for Juneau are as follows:
Mean Tide Range 13.8 ft.
Diurnal Tide Range 16.4 ft.
Flood Current (strength) 2 knots at 315 degrees True
Ebb Current (strength) 2 knots at 135 degrees True
Spot checks of tide height at a dockside staff gage during this study
showed actual tide heights and times closely approximated those
predicted. Observed times of slack and strength current agreed fairly
well with those predicted, although measured velocities were erratic
and slightly less than predicted values.
Currents measured at Stations 1 and 2 are shown on Figures 1-5B
and 1-6B, respectively. Velocities are shown full value as observed
in either flood (northwesterly or up-channel) or ebb (southeasterly
or down-channel) direction without regard to specific direction
measured. Current direction at Station 1 was generally oriented up-
or down-channel without much cross-channel tendency. Current
direction at Station 2 had an intermittent set toward Douglas Island,
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apparently due to eddy action in the expanded channel section of Juneau
harbor. Surface currents at both stations were stronger than those
measured at depth.
Strength of flood and strength of ebb near-surface current
patterns are shown on Figures 1-7 and 1-8, respectively, as composited
from current measurements and the several float studies made in the
area. Floats released under the bridge on a flood tide consistently
moved toward the Juneau shore, occasionally entering the boat basin
through its northwest entrance. Floats released under the bridge
during either flood or ebb tide did not move completely out of the
Juneau-Douglas study area (Figure 1-2) during a single tidal excursion.
A flood tide release of Rhodamine dye under the bridge near
the Douglas Island side moved quickly cross-channel and flooded up
along the Juneau shore. Much of the dye moved into the boat basin
through its northwest entrance, with the remainder eventually moving
around the entrance jetty and up-channel along the Juneau shore.
Dye released as a continuous line between the bridge piers on an ebb
tide moved mainly down-channel as expected but with some up-channel
movement by eddies near each shore. The main portion of the dye
disappeared into several tide tips as it reached the expanded channel
section. Fluorometric monitoring of this dye release after low water
slack showed considerable quantities of dye along the Juneau shore in
the expanded channel section. Sketches of successive dye positions
are shown on Figures 1-9 and 1-10 for both the flood and ebb dye
releases, respectively.
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Salinity-Freshwater Relationships. Salinity measurements with
depth showed considerable depression of near-surface salinities,
apparently from widespread melting of snow and glaciers throughout the
Stephens Passage area, rather than from local sources in Gastineau
Channel. Annual cycles of salinity, temperature, and dissolved oxygen
distributions with depth are shown in Figure 1-11 for a station in
outer Auke Bay (Figure 1-1), based on data provided by U. S. Bureau
of Commercial Fisheries, Auke Bay Laboratory. The figure indicates
that conditions of extensive surface layering of fresh water prevails
from June through September.
Observed longitudinal salinity distribution in Gastineau Channel
near high water slack on August 20 is shown on Figure 1-12.
Salinities, temperatures, and the resultant densities (in terms of
specific gravity) for Station 1 on August 17 and Station 2 on
August 18 are shown on Figures 1-5C, D, and E, and 1-6C, D, and E,
respectively. Some features noticed in comparison of these graphs
are:
a. Layering of fresher water near the surface is generally
prominent to depths of 5-10 meters.
b. A definite tendency of surface salinity to increase
toward the upper end of Gastineau Channel (Figure 1-12)
indicates that the major source of the observed fresh
water is from Stephens Passage, rather than from up-
channel sources.
c. Higher surface salinities on the ebb than on the flood at
Station 2, and a corresponding reduction in density
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stratification (Figure 1-6C and E), indicate mixing of the
water column in the area up-channel from Station 2. This is
probably due both to local mixing through the channel
constriction under the bridge area and to general mixing in
the tide flat areas of upper Gastineau Channel. Since a
similar trend is not as prominent at Station 1 (Figure
1-5C and E), it appears that a significant portion of the
mixing occurring up-channel from Station 2 occurs in the
area between Stations 1 and 2.
One of the effects of increased surface salinity in the bridge
area is to produce tide-rips whenever a mass of heavier water
(more saline) meets with a mass of lighter water (less saline). The
heavier-water sinks under the mass of lighter water to produce tide
rips at the interface. Several tide-rips were noticed in Gastineau
Channel, particularly immediately above the bridge during the first
part of the flood tide and below the bridge during the first part of
the ebb tide. Current floats would not cross a tide-rip but would
travel rapidly along it, resulting in a congregation of floats at the
end of the rip. Surface dye was observed to sink at the rip as
previously noted.
Net Circulation. In a long, narrow tidal channel, such as
Gastineau, closed at one end and open to the sea and tides at the
other, there is generally no net transport provided by the tidal
currents. Water leaving the channel on the ebb tide equals that
entering on the flood tide, with no net predominance either into or
out of the channel. However, freshwater entering the channel from
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local sources (rivers, creeks, glacier melt, rain, etc.) lies near the
surface and must eventually move to sea, producing a net outflow near
the surface of the tidal channel. Saline water from depth which mixes
with this freshwater, and is eventually carried outward with it, must
be replaced by a net inward motion at depth. The extent to which this
two-layer system develops and the rate at which the net motion proceeds
depends on channel geometry, tides, and freshwater discharge. Review
of surface water data published by U. S. Geological Survey (1) shows
that local runoff to upper Gastineau Channel is minor when compared to
the tidal flow, thus indicating that net seaward motion due to fresh-
water inflow is also minor.
Based on the salinity observations previously discussed, it is
evident that a significant freshwater layer was present in Gastineau
Channel during the time of measurement. The major freshwater source,
however, was from the seaward end of the channel, rather than from
within the channel. Sinking of the heavier water mass created by
mixing above Station 2, and subsequent inward spreading of the fresher
layer over it, provides a mechanism whereby net motion in Gastineau
Channel may actually be inward at the surface and outward at depth.
Current readings at Station 2 (Figure 1-6B) were too erratic to
reliably describe such a motion, but those at Station 1 do exhibit a
tendency for flood direction predominance at the surface and ebb
direction predominance at depth. However, since the channel becomes
quite shallow immediately above Station 1, this point would be near
the upper limit of such a net circulation.
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One other factor which could affect net circulation in Gastineau
Channel is the possibility of a significant tidal exchange through the
tide flat area between upper Gastineau Channel and Fritz Cove.
Examination of current meter data collected in the small navigation
channel through this area in 1963 by U. S. Geological Survey (5)
indicates that a nodal point of no-net-flow does occur, thus
minimizing the probability that flow to or from Fritz Cove (and
Mendenhall River) is a significant factor in Gastineau Channel
circulation.
WATER QUALITY
Dissolved Oxygen. Dissolved oxygen content in natural waters
may be increased through surface reaeration and phytoplankton
productivity (during sunlight) and decreased by organic demands and
plankton respiration (during darkness). Since the only mechanism
for increasing dissolved oxygen occurs at or near the surface,
dissolved oxygen normally decreases with depth, particularly in a stably
stratified water mass where vertical mixing is slow. Near-surface
coastal waters are often super-saturated with DO in the spring and
summer due to plankton productivity stimulated by nutrients, sunlight,
and elevated water temperature. DO values usually drop during the fall
and winter when nutrient supply decreases (from productivity), sunlight
and water temperature decrease, and some oxygen demand is exerted by
oxidation of the dead plankton population. Another significant factor
affecting the dissolved oxygen content of Pacific coastal waters is
the upwelling which occurs along the outer coast during spring and
summer due to coastal winds. Surface waters transported offshore are
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replaced nearshore by high salinity, low oxygenated water from depth.
By virtue of its higher density, this upwelled water slowly spreads at
depth into the coastal bays, sounds, inlets, etc., and is initially
manifested in the inner reaches by late summer or early fall as high
salinity and low oxygen concentration near the bottom. Slow mixing
thereafter results in generally depressed oxygen conditions throughout
the water column during late fall and winter. The essential features
of such a typical annual DO cycle are noticeable at the Auke Bay
station as illustrated on Figure 1-11C.
Dissolved oxygen concentration at the two-meter depth in Gastineau
Channel, monitored between Thane and Juneau boat basin (see Figure 1-1)
near low water slack on August 19, varied between 10070 and 112%
saturation with most of the readings at 104-106%. No particular trend
was observed as far as longitudinal distribution was concerned. DO
was generally at or above saturation at depths less than 5 meters.
DO concentrations observed over the tide cycle at Stations 1 and 2
are shown on Figures 1-13B and C and 1-14B and C, respectively. One
notable feature of these distributions is increased DO concentration at
depth during ebb current, an indication of mixing up-channel from both
stations.
pH. pH of Pacific coastal waters varies between about 7.5-8.5
depending on depth, time of year, etc. Seawater is considerably
buffered against pH changes but can be altered by both dilution from
freshwater inflow and by addition or depletion of C02 through
atmospheric interchange or biologic activity. An addition of C02, such
as during plankton respiration, decreases the pH of seawater; while
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depletion of C02, such as during plankton productivity, increases
the PH.
pH values observed over the tidal cycle at Stations 1 and 2 are
shown on Figures 1-13D and 1-14D, respectively.
Bacterial Quality. Raw sewage is presently discharged into
Gastineau Channel from numerous outfalls located principally in the
immediate waterfront areas of the cities of Juneau and Douglas
(Figure 1-4). The presence of this raw sewage in the immediate
waterfront areas represents a potential health hazard to those working
on, and who have contact with, the water.
On August 23, some 25 samples were collected at low tide from
stations in Gastineau Channel and analyzed for the presence of those
bacteria associated with human wastes. Stations sampled are indicated
on Figure 1-3. Results of these analyses, which are tabulated below,
indicate that MPN's in excess of 1,000/100 ml occur at most stations
located in the active waterfront areas. The Division of Public Health
of the State of Alaska, Department of Health and Welfare, recommends
that MPN not exceed 1,000/100 ML for waters used for boating, fishing,
and related commercial activities.
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BACTERIOLOGICAL RESULTS
August 23, 1965
Sampling
Station
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
MPN's
per 100 ml
240
240
240
240+
240
240+
380
240+
2,400+
2,400
2,400+
2,400+
150
88
2,400
2,400
15
2
240+
38
2,400+
2,400
960
240+
150
15
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CONCLUSIONS AND RECOMMENDATIONS
CONCLUSIONS
The salinity-freshwater relationships prevailing during the study
period were not representative of winter conditions. However, there
are several pertinent factors which have been described:
1. Significant mixing occurs between Stations 1 and 2,
which would enhance initial waste dispersion from a source
in this area.
2. Flood current past the restricted portion of the channel near
the bridge favors the Juneau shoreline, resulting in
considerable circulation of main channel water through the
boat basin.
3. Local eddies are formed near both the Juneau and Douglas
Island shorelines adjacent to the bridge, and during ebb
current in the main channel carry water up-channel along
both shores.
*
4. Large eddies exist in the expanded section down-channel from
the bridge during both flood and ebb current.
5. Net transport out of the channel is very slow with a slight
tendency for inward surface motion to the bridge area during
the summer.
Some general statements may be made concerning Gastineau Channel
circulation in the absence of fresher surface waters from Stephens
Passage, descriptive of winter conditions:
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1. Local flood and ebb current patten _ ...id eddies would remain
basically unchanged except for tide-rip Activity which should
diminish.
2. Mixing near the bridge would increase slightly, due to
lessening of density stratification.
3. Net circulation would continue to be very slow but with some
slight near-surface movement seaward due to local freshwater
inflow.
RECOMMENDATIONS
Outfall Location. In order to best take advantage of the above
factors in minimizing the effects of waste effluents on the waters of
Gastineau Channel, the following recommendations are made:
1. Locate the outfall down-channel from the bridge about midway
between the bridge and the expanded channel section.
Preference should be given to the Juneau shore, but considera-
tion of a Douglas Island site may be given subject to 2. below.
2. The terminal end of the outfall should extend at least 100 feet
beyond the nearshore eddy limits to minimize local concentra-
tion of effluent along the shore. Based on the studies,
estimated location of the terminal end would be at the 40 foot
depth contour (referenced to mean lower low water). This
submergence would contribute significantly toward initial waste
dispersal due to mixing of the buoyant waste plume as it rises.
The above recommendations envision at least a primary treated effluent
with chlorination. Any compromise selection of the outfall site due to
construction costs, right of way, etc., should include consideration
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of a higher degree of treatment, or be based on further study of
the area.
Follow-up Studies. Before final site selection and outfall and
treatment plant design are made, the following investigations should
be undertaken:
1. Determine the exact limits of any nearshore eddy at the
outfall site selected. This should be done for both flood
and ebb current and could be accomplished using either floats
or dye.
2. Determine the path of flood and ebb tidal excursion from
the selected outfall site. This could be accomplished by
releasing floats or dye over the outfall site at slack current
and monitoring subsequent water movement until the following
slack.
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LEGEND
C
• Data station; salinity Q tem-
perature measurements, Aug. 20,1965
I (Continuous monitoring traverse;
dissolved oxygen, pH, salinity
Q temperature at two meter
depth. Aug.19, 1965
(•) Data station; U.S. Bureau of
Commercial Fisheries,
salinity, temperature and
dissolved oxygen.
Mar. 1963 -Feb. 1964
DOUGLAS Si. AN/D
rTGURE 1-1. Gastineau Channel area and sampling locations,
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••••-.. II •.
BRIDGE
LEGEND
1
A Location of data measure
ment station; station 1
occupied from II3O-23OO
hours on Aug. 17, I965 &
station 2 occupied trom
IOOO-22OO hours on Aug.
IS, 1965
12 Soundings in fathoms below
MLLW
FIGURE 1-2. Juneau-Douglas area of Gastineau Channel and sampling locations.
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BOAT
BASIN
J HJ
58°
20"'
II •
12 13
• '6
17
18
25'
20
24-
1/2
• 23
FIGURE 1-3. Bacteriological sampling locations - August 23, 1965.
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FIGURE 1-4.
Raw sewage outfall locations; information provided by State of Alaska
Department of Health and Welfare,
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12
I
TIME IN HOURS AUG. 17, 1965
14 16 18 2O
I I I I
22
I
24
H
Ul
ill
u.
o
UJ
10-
ML LW
(A) PREDICTED TIDE
s * ••-
O O
i 3
u.
z 0-
2: «
h- 0)
<5 XJ I -
I I
Surface
IB.) CURRENT VELOCITY
CO
a:
UJ
UJ
2
a.
0-
10-
20-
- --3O.
(OSALINITY IN PARTS PER THOUSAND
V)
ce.
UJ
UJ
fc
ui
o
0.
10-
20— '
/^° ^<»
m^— "^.^
' • *-- "77" ^~ — -^
en
gj
u
UJ
o
•CE.) SPECIFIC GRAVITY
FIGURE 1-5. Patterns of (B) current velocity, (C) salinity, (D) temperature and
(E) specific gravity observed at Station 1 on August 17, 1965.
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10
TIME IN HOURS AUG.18,1965
12 14 16 18
I I I I
20
I
22
HI
u.
l-
o
UJ
I
10-
0-
MLLW
(A)PREDICTED TIDE
ul 4
I6meter depth (52 ft.)
CURRENT VELOCITY
V)
K
Ut
H
Ul
o.
UJ
o
(O
K
UJ
2
Z
I
h-
Q.
UJ
O
UI
UJ
z
2
T.
O.
UJ
a
0-1
10-
20-
30-
OH
10-
20-
30-
(C)SALINITY IN PARTS PER THOUSAND
ID) TEMPERATURE IN °c
I.OI3
IE) SPECIFIC GRAVITY
FIGURE 1-6. Patterns of (B) current velocity, (C) salinity, (D) temperature
and (E) specific gravity observed at Station 2 on August 18, 1965.
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\ »,v
LEGEND
•
Sp««d in knots and direction
of surface current
FIGURE 1-7. Strength od surface current rn based on float studies
conducted August 18-20, 1965.
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LEGEND
Speed in knots and direction
of surface current
Dougl,
FIGURE 1-8.
Strength of ebb surface current pattern based on float studies
conducted August 18-20, 1965.
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O IOO 2QO 3OO
YARDS
BOAT
BAS IN
JJ IL) NM IE A\ II)
Sequence
1
2
3
4
5
6
7
8
9
Approx.
Tim*
II2O
1125
II3O
II4O
II 5O
I2O5
I22O
I24O
1430
JUNEAU-DOUGLAS I.
BRID GE
Mean lower low/
water
FIGURE 1-9. Sketch of successive positions of a surface dye-release during
a flood tide on August 17, 1965.
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J) ILJ Nl IE A\ UJ
JUNEAU-DOUGLAS I
BRIDGE
too o too zoo 300
I ! HZZ
Mean lower low water
FIGURE 1-10. Sketch of successive positions of a surface dye-release during
an ebb tide on August 20, 1965.
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1963 1964
MAR APR MAY JUN JUL AUG SEP OCT NOV DEC JAN FEB
FIGURE 1-11. Annual cycles of (A) salinity, (B) temperature and (C) dissolved
oxygen for a sampling station in outer Auke Bay; data provided by U. S. Bureau
of Commercial Fisheries.
-------
0
10
20
30
a.
UJ
Q 50
JUNEAU-DOUGLAS L
BRIDGE
0 I
NAUTICAL MILES FROM BRIDGE
up Channel
down channel
No
_^NO I —
~Oata ~~ ~~ r~ ""
2O -1
BOTTOM OF GASTINEAU CHANNEL
STEPHENS
PASSAGE
FIGURE 1-12. Observed pattern of salinity distribution in Gastineau Channel near high-water slack on
August 20, 1965.
-------
12
I
TIME IN HOURS AUG. 17, 1965
14 16 18 2O
III!
22
I
24
I
ui
Ul
u.
o
20-
10-
0-
(A) PREDICTED TIDE
cc
u
H
Ul
X
H
0.
u
o
0-
10-
20-
10 DISSOLVED OXYGEN IN Mg/L
* o-
H
Ul
2 10-
z
H 20-
Q.
0
a.f e.4
«--*^^ > 7 g >. ^ _
1
(D)nH
FIGURE 1-13. Patterns of (B) dissolved oxygen in percent saturation, (C) dissolved
oxygen in milligrams per liter, and (D) pH at Station 1 on August 17, 1965.
-------
10
I
TIME IN HOURS AUG. 18, 1965
12 14 |6 |8
I I I I
2O
I
22
I
to
(E
UJ
ui
5
20-
X
t-
son
(O
(C
tu
h-
UJ
2
0-
10-
f 20-
0.
ui
Q
30-
o:
ui
*-
ui
as
X
0
10-
20-
30-
(A)PREDICTED TIDE
I2O
(B)DISSOLVED OXYGEN IN % SATURATION
(ODissoLVED OXYGEN IN Mg/L
tO)pH
IGURE 1-14. Patterns of (B) dissolved oxygen in percent saturation, (C) dissolved
oxygen in milligrams per liter and (D) pH' at Station 2 on August 18, 1965.
-------
CHAPTER 2
FRITZ COVE STUDY
August 21-25, 1965
-------
STUDY OBJECTIVES
Objectives of the Fritz Cove field studies were to determine
water circulation and water quality patterns which would be pertinent
to consideration of the area as a possible pulp mill location site.
The field studies were designed to give primary consideration
to three critical points:
1. Describe basic tidal circulation in the Cove.
2. Describe current and water quality patterns in the
southeastern corner of the Cove. This was considered to
be the most likely area of initial consideration for
location of the proposed pulp mill.
3. Determine if wastes discharged into Fritz Cove would also
circulate into Auke Bay.
19
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AREA DESCRIPTION
Fritz Cove is a semi-enclosed embayment of Stephens Passage
situated between the mainland and Douglas Island (see Figure 1-1)*
Depths vary from about 110 meters at its entrance connection with
Stephens Passage to the extensive exposed inner tideflats separating
Fritz Cove from Gastineau Channel. Depth contours are shown on
Figure 2-1. The approximate surface area of the Cove at low tide is
2.5 square miles. There is a small mid-cove connecting channel into
Auke Bay. The combined surface area of Fritz Cove and adjacent Auke
Bay is about 9 square miles.
Fritz Cove receives freshwater discharge from both Mendenhall
River and Fish Creek (Figure 2-1). Mendenhall River flow varies from
wintertime base flows of about 100 cfs (1) to summer freshet mean
daily flows of at least 6,900 cfs (4). Summer freshets are associated
with melting of snow and ice from Mendenhall Glacier located about
4 miles upstream from Fritz Cove. Fish Creek flows vary from winter
base flows of less than 10 cfs to maximum mean daily flows exceeding
600 cfs (1).
"Figures follow page 31
20
-------
STUDIES
Primary efforts were devoted to describing water circulation
patterns in Fritz Cove.
A sampling station was occupied over a 12-hour tidal cycle on
August 21, 1965, at the location shown on Figure 2-1. Station
location was selected as being in the most probable area of initial
consideration for a pulp mill outfall site. Measurements of salinity,
temperature, DO, and pH were made at hourly intervals at the surface
and the 2, 5, 10, 20, and 40 meter depths. Observations of current
speed and direction were made at approximately half-hourly intervals
at the surface and the 8, 16, and 24 meter depths.
Salinity and temperature at the surface were measured at 19
locations in Fritz Cove at high water slack on August 23 to describe
the horizontal distribution of freshwater. Vertical distributions of
salinity and temperature at 4 stations along a longitudinal mid-bay
transect (Figure 2-1) were measured at both high and low water slack
on August 24.
Current float studies were conducted in Fritz Cove on August 21,
23-25. Drogues were released at various locations and depths during
both flood and ebb tides.
A surface release of Rhodamine B dye was made at the inner end of
Fritz Cove on August 22. Subsequent dye distribution patterns were
monitored in the Fritz Cove-Auke Bay area on August 23-24. A similar
release was made on August 24 and monitored on August 24-25.
21
-------
METHODS
All methods used in the Fritz Cove studies were essentially the
same as those previously described for the Gastineau Channel
investigations (see Chapter 1).
22
-------
RESULTS
WATER CIRCULATION
Mendenhall River was in freshet condition during the period studies
were being conducted in Fritz Cove. Glacial melt water from the river,
apparent by its light color, was at times distributed in a thin surface
layer which appeared to move seaward almost independent of the tide
motion.
Tides and Tidal Currents. Daily tide predictions for Fritz Cove
are listed by U. S. Coast and Geodetic Survey (3). The mean and
diurnal tide ranges are 13.5 feet and 15.9 feet, respectively. Examina-
tion of U. S. Geological Survey tidal observation data (5) shows actual
tides to be essentially as predicted. Current predictions are not
listed for Fritz Cove.
Currents measured at the Fritz Cove sampling station were slow and
very erratic at all depths, and appeared to result from variable
nearshore eddies. Current velocity at the surface and 8 meter depth
did not exceed 0.2 knots. Deeper velocities were mostly under 0.05
knots. No discernible pattern of either speed or direction was evident
at any depth.
The accelerated outflow effect of freshet waters near the surface
in Fritz Cove occurs for only a relatively short period each year
(weeks) and was not considered representative of conditions which would
be critical to location of a pulp mill waste outfall. For this reason
most float studies were conducted at the 3-meter depth to better
approximate basic tidal circulation.
23
-------
Tidal circulation in Fritz Cove is effected by filling and
emptying tidal currents, freshwater discharge, and tidal currents
in Stephens Passage. These factors, coupled with a wide and deep
basin geometry and a middle connection to Auke Bay, result in tidal
circulation characterized by slow, wandering currents which vary with
depth. Migrating tide-rips, with considerably different water motion
on each side, were frequently observed on the southern side of the
Cove during a change in tide.
Although a predominant flood or ebb pattern was not particularly
well-defined at any given time, composite estimates of such patterns
were possible on the basis of several float studies. These are shown
for a "strength of flood" and "strength of ebb" condition at the
3-meter depth on Figures 2-2 and 2-3, respectively. Currents at
8-meter and 16-meter depths had essentially the same pattern but less
than half the speed.
A true slack tide condition did not develop in the Cove. Rather,
currents would wander from one basic pattern to the next over the tide
change. The current pattern change took an hour or more to develop
and lagged the high or low tide height by one or two hours. This is a
shift toward the tidal current timing in Stephens Passage. Based on
U. S. Geological Survey data (5), tidal currents in the Fritz Cove
portion of the tide flat connection to Gastineau Channel slack and flow
essentially with the timing of the tide.
One notable feature of the current patterns (Figures 2-2 and 2-3)
is that currents along the inner quarter of the southern shore are
predominantly inward during both flood and ebb tide conditions.
24
-------
Salinity-Freshwater Relationships. Near-surface salinities in
Fritz Cove were extremely variable, both from time-to-time and
place-to-place, due to Mendenhall River freshet condition and the
wandering nature of the tidal currents. Freshet waters were detectable
in the Cove to some extent by color and by depression of surface
salinity below the minimum of about 13 parts per thousand observed in
Stephens Passage. The Mendenhall River plume was observed most
frequently on the northern (ebb) side of Fritz Cove and was generally
layered above 2 meters in depth. Vertical salinity distribution below
the 2-meter depth did not greatly reflect that lying above it.
Salinity, temperature and density observed at Station A for the
12-hour period on August 21 are shown on Figure 2-4. The surface
salinity pattern in Fritz Cove as measured at high tide on August 23
is shown on Figure 2-5. High and low tide vertical salinity distribu-
tions as measured along a mid-Cove transect on August 24 are shown on
Figure 2-6. These patterns are considered representative of conditions
during high Mendenhall River runoff. An annual cycle of salinity and
temperature for a station in nearby Auke Bay was shown in Chapter 1
(Figures 1-1 and 1-11B and C).
Net Circulation. Net transport of surface waters in Fritz Cove
must be seaward due to the Mendenhall River inflow. Based on salinity
observations this effect is most prominent along the northern side of
the Cove. Beneath the fresher layer during periods of high Mendenhall
River discharge (summer), and for all waters in the Cove in the absence
of high discharge (winter months), any net transport must result
primarily from tidal or wind driven circulation. Some indication of a
25
-------
net inward predominance of tidal currents near the southern shore at
the inner end of the Cove was noted from the 3 meter depth float
studies (Figures 2-2 and 2-3).
Successive dye patterns observed following the surface releases
of Rhodamine B at the inner end of the Cove on August 22 and 24 are
shown on Figures 2-7 through 2-9 and 2-10 through 2-12, respectively.
Contour values shown are in fluorometer units which approximate relative
dye concentration. Absolute concentration could not be defined because
of variable background readings due to suspended particles in the water.
This background varied from 5 to 25 fluorometer units in Stephens
Passage and Mendenhall River, respectively. Background values monitored
at the surface in Auke Bay prior to the dye releases were less than
10 fluorometer units, with some apparent effect from suspended particles
in Auke Creek discharge. Any dilution of freshwater discharge with
seawater would cause a corresponding reduction in background reading.
Some features noticed in examination of the dye sketches
(Figures 2-7 through 2-12) are:
1. Water from the inner end of Fritz Cove is not completely
replaced each tidal cycle but is moved out in patches over a
period of several tidal cycles.
2. Initial displacement of the patches from the inner end of the
Cove is counterclockwise, followed by primary movement
outward along the northern side of the Cove to mid-bay.
Final movement out of the Cove is predominantly back toward
the southern shore as suggested by the ebb current pattern
(Figure 2-3).
26
-------
3. Dye was definitely still present in Fritz Cove after about
4 tidal cycles (August 22-24).
4. Fluorometer readings in Auke Bay following both dye releases
were above natural background values expected. Those shown
on Figures 2-11 and 2-12 (August 24 dye release) are
considered definite indication of dye movement from inner
Fritz Cove into Auke Bay.
Dye movements shown should be considered representative of surface
conditions during Mendenhall River freshet periods. Rate of net
transport during other periods and at depth at all times would be
reduced.
WATER QUALITY
Dissolved oxygen content, in terms of percent saturation and
milligrams per liter, and pH values measured at Station A on August 21
are shown on Figure 2-13. An annual cycle of dissolved oxygen for a
station in nearby Auke Bay was presented in Chapter 1 (Figure 1-11).
27
-------
CONCLUSIONS AND RECOMMENDATIONS
CONCLUSIONS
Physical conditions in Fritz Cove during this study were
representative of a relatively short period of the annual cycle,
particularly with respect to the observed accelerated surface outflow
due to Mendenhall River freshet discharge. However, certain general
features of Fritz Cove were described which are important to
consideration of the area as a possible pulp mill effluent receiver:
1. Tidal circulation in Fritz Cove is slow and wandering with
most of the motion occurring near the surface. Inside the
Cove, flood motion appears strongest along the southern side
and ebb motion appears strongest toward the northern side.
2. A counterclockwise eddy develops at the inner end of the Cove
during ebb tide; thus, transport is directed predominantly
inward along the inner southern shore during both flood and
ebb tides.
3. Water from the inner end of the Cove is not completely
exchanged in a single tidal cycle but is circulated in the
Cove and flushed outward over a period of days.
4. Wastes discharged to surface waters within the Cove would
eventually disperse into Auke Bay.
In addition, the annual cycle of salinity and temperature
(Figure 1-11A and B) indicates that the area waters are stably
stratified (density increases significantly with depth) during the
28
-------
period from about May to October and are near-neutral or unstable
during the remainder of the year. A stable stratification inhibits
vertical mixing and would tend to confine surface-discharged wastes
near the surface and deep-discharged wastes at depth. Conversely, a
neutral or unstable condition facilitates vertical mixing of the
water column.
Consideration of Fritz Cove as a possible location for a pulp
mill must include evaluation of its potential effect on marine
resources of the area. One aspect of primary importance in the Fritz
Cove-Auke Bay area is the presence of the U, S. Fish and Wildlife
Service, Bureau of Commercial Fisheries Laboratory, located on Auke Bay.
This laboratory engages in important comprehensive basic and applied
fisheries research programs in Fritz Cove-Auke Bay and adjacent waters.
Presence of pulp mill pollution in the area may jeopardize much of the
laboratory's potential and invalidate considerable portions of basic
programs already under way.
Sulfite waste liquor (SWL) concentration is generally used as an
indicator of the presence of pulp mill wastes in natural waters.
Bioassay studies conducted recently by this office in conjunction with
investigations of pulp mill pollution in Puget Sound, Washington, show
that the marine biota is adversely affected by relatively low
concentrations of SWL. Concentrations of 10 ppm result in a 12 percent
mortality to oyster larvae.
Average SWL content in pulp mill effluent varies from about
5,000 ppm from a mill employing chemical recovery to more than 200,000 ppm
from a mill with no recovery. For example, main sewer effluent from
29
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the Ketchikan Pulp Company mill at Ward Cove (described in Chapter 4)
during a three-day study period averaged 34.4 million gallons per day at
an SWL concentration of 7,285 ppm. If this waste were discharged and
uniformly mixed within Fritz Cove it would be sufficient to raise the
SWL concentration above the 10 ppm toxicity threshhold in a surface
layer 10 feet deep within the first 5 hours of plant operation. There
are numerous examples of the far-reaching effects of pulp mill wastes
discharged to embayed coastal waters similar to those of the Fritz Cove-
Auke Bay embayment of Stephens Passage:
1. Ward Cove near Ketchikan, Alaska, where SWL concentrations
from the Ketchikan Pulp Company mill were observed at the
surface between about 500 and 1,000 ppm within Ward Cove, up
to one mile from the source, and between about 20 and 40 ppm
in the adjacent waters of Tongass Narrows, more than two miles
from the source (see Chapter 4).
2. Silver Bay near Sitka, Alaska, where SWL from the Alaska
Lumber and Pulp Company mill was observed to generally exceed
200 ppm at the surface throughout an area of at least 10
square miles. SWL concentrations exceeding 250 ppm were
observed about 3 miles from the source (see Chapter 3).
3. Everett, Washington, where combined wastes from Scott Paper
Company mill and Weyerhaeuser Corporation mill are discharged
to Port Gardner via a deep diffuser. SWL concentrations in
the receiving waters have been observed to average over
30 ppm at a distance of 10 miles from the source.
30
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4. Bellingham-Samish Bay, Washington, where SWL concentrations
from the Georgia-Pacific Corporation pulp mill have been
observed in surface waters to exceed 50 ppm at a distance of
8 miles from the source. Average SWL concentrations exceed
200 ppm over a one-square-mile area and 10 ppm over a fifty-
square-mile area.
In addition to toxic effects of pulp waste on marine biota,
serious water quality degradation, in terms of reduced dissolved oxygen
lowered pH, increased color, etc., usually occurs in natural waters
due to the presence of such wastes (for example, see Chapters 3 and 4).
In view of (a) the apparent slow tidal circulation and lack of
strong net transport of water away from the area, (b) the demonstrated
dispersion of Fritz Cove water into Auke Bay, and (c) the comparable
size of the approximately 9-square-mile Fritz Cove-Auke Bay system to
other areas affected by pulp mill waste discharge, it is expected that
discharge of pulp mill wastes within Fritz Cove would result in
occurrence of waste concentrations well above the toxicity threshhold
throughout the Fritz Cove-Auke Bay area.
RECOMMENDATIONS
Based on the foregoing discussion and in the interest of
preserving the research potential of the Auke Bay Laboratory, it is
recommended that another area be sought for location of a future pulp
mill outfall.
If an alternative site is not available and Fritz Cove is
selected, we recommend that consideration be given only if subject to
the following:
31
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1. The outfall be located in Stephens Passage outside the limits
of circulation in the Fritz Cove-Auke Bay embayment. This
should be considered only if it can be established that there
is a significant net transport away from the selected site
sufficient to insure dilution of waste concentration below
threshhold values in any area deemed important to the marine
resources.
2. The outfall be equipped with a diffuser section designed
for maximum initial dilution and submerged to the depth
necessary to insure containment of the buoyant waste plume
below at least 30 meters depth during all degrees of density
stratification likely to occur.
32
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EGEND
MLLW
io- Depth contours in meters,
referenced to MLLW
4 Data measurement station;
O occupied from O8OO to ZIOOhrs.
on Aug. 21.1965
2 Data station. High tide-Low tide
A salinity and temperature transect
a Aug. 24. 1965
FIGURE 2-1. Fritz Cove study area and sampling locations
-------
/J\
\
0.5
0.2
o
/ O.I
05
O.I
O.O5
'
LEGEND
g Speed in knots and direction
t^' of currant at 3 meter depth
• / 1
NAUTICAL. M I t,
FIGURE 2-2. Estimated strength of flood current pattern at three meter depth,
based on float studies conducted August 21, 23-25, 1965.
-------
A
/
\
\
0.3
0.3
0.2
0.05
LEGEND
02 Speed in knots and direction
''of current at 3 meter depth
i/ »
NAUTICAL. Mil.*
FIGURE 2-3.
Estimated strength of ebb current pattern at three rneter depth, based
on float studies conducted August 21, 23-25, 1965.
-------
TIME IN HOURS AUG.21,1965
8 9 10 II 12 13 14 15 16 17 IB 19 20 21
I I I I I I I I I I f I | |
UJ
UJ
u.
z
—
UJ
X
10-
0-
MLLW
' ' ' '
(A) PREDICTED TIDE
UJ
t-
Ul
2
I
1-
0.
UJ
Q
0-
10-
20-
30-
40-
/O
to
>2O-
•25
<33
IB) SALINITY IN PARTS PER THOUSAND
IT
UJ
&
UJ
o
o:
UJ
UJ
X
a,
UJ
o
40-1
tc) TEMPERATURE IN °c
I.OI5\
0 —
10-
20-
30-
40-
/ OIO I.OIO I.O05 \ I.OIO
_ i i i i i i ii i-
-------
^
\
> A
10
LEGEND
S ur f oc« *o 11 n i ty in
f ports per thousand
FIGURE 2-5. Pattern of surface salinity at high water slack, August 23, 1965.
-------
2.0
Nautica I Ml les
I .5 I .0 0.5
10
20
30
40
Q.
tt)
Q
0
10
20
3C
4C
i Salinity
ITransect
j M
j \^^
CVJ ^
OGOO
LJ
10
I 0
T
TIME
I 200
I
1800
MLLH
Predicted Tide
FIGURE 2-6. Vertical salinity patterns along a mid-Cove transect at (A) high
water slack and (B) low water slack, August 24, 1965.
-------
30
LEGEND
-«/
. App roximate relative dye
20 concentration in terms of
arbitrary fluorometer units -,
values less than lOunits are
considered natural background.
Dye release point; 3gallonsot
rhodamine dye released at
surtace at I2OO hours. Aug. 22, 1965
PACIFIC STANDARD TIME
I2OO Z400 I ZOO 24 OO 1200
|
T 10
MT>it
NAUTICAL MIL.B
Aug
Aoi) 2S Au) 24
FIGURE 2-7. Surface dye dispersal pattern observed between 1030 and 1200 hours
on August 23, following August 22 dye release.
-------
ao1
LEGEND
^ Approximate relative dye
20 concentration in terms of
arbitrary fluorometer units;
values less than IO units are
considered natural background.
Dye release point; three gallons
rhodarnine dye released at surface
at I2OO hours, Aug.22, 1965
PiClflC STANDARD TIME
1200 2400 1200 2400 1200
NAUTICAL. MIL.
AugZJ
FIGURE 2-8. Surface dye dispersal pattern observed between 1830 and 1930 hours
on August 23, following August 22 dye release.
-------
-------
L\o
A
PACIFIC STANDARD TIME
1200 2400 I2OO 2400
LEGEND
..Approximate relative dye
20 concentration in terms of
arbitrarary flourometer
units; values less than IO
units are considered nature
background.
^ Dye release point; 7ga I Ions
rhodamine dye released at
surface at I2OO hours,
August 24,1965
LU 0
a
Y
Dye released pye observed
NAUTICAL
I U K
ULLW
Aug.24
Aug.25
FIGURE 2-10. Surface dye dispersal pattern observed between 1930 and 2100 hours
on August 24, following August 24 dye release.
-------
PACIFIC STANDARD TIME
I2OO 2400 1200 2400
Approximate relative dye
concentration in terms of
arbitrary fluorometer units;
values less than IO units are
considered natural background.
Dye release point; Tgallons
rhodamine dye released at
surface at I2OO hours,
Aug.24,1965
M I U C
Aug.25
FIGURE 2-11. Surface dye dispersal pattern observed between 0830 and 0930 hours
on August 25, following August 24 dye release.
-------
10
Ul
I
V
J
7
Vf L
rx.i8
r
PACIFIC STANDARD TIME
1200 2400 I2OO 2400
released
LEGEND
Approximate relative dye
j concentration in terms of
arbi tra ry f I uo rometer units;
values less than lOunits are
considered natural background.
Dye release point; 7gallons of
rhodamine dye released at
surface at !2OOhours
Aug.24, 1965.
i/ a
N A U T I C A
ULLW
Aug. 24
Aug.25 Dye observed
FIGURE 2-12. Surface dye dispersal pattern observed between 1830 and 1930 hours
on August 25, following August 24 dye release.
-------
TIME IN HOURS AUG.21,1965
9 10 II 12 13 14 15 16 17 18 19 20
I I I I I I I I I I I I
UJ
UJ
u.
X
CD
UJ
X
v>
er
UJ
H
UJ
3
Q.
Ul
O
10-
0-
0-
10-
20-
30-
40-
(A)
7O
MLLW
PREDICTED TIDE
IOO
7O
70
70
18) DISSOLVED OXYGEN IN % SATURATION
UJ
H
UJ
Z
0.
UJ
O
0-
10
20-
30-
40-
>7
to DISSOLVED OXYGEN IN
a:
ui
H
UJ
•s.
0-
10-
20-
t 30H
UJ
o
8.4
8.4
8.4
FIGURE 2-13. Patterns of (B) dissolved oxygen in percent saturation, (C) dissolved
oxygen in milligrams per liter, and (D) pH at sampling Station A, August 21, 1965.
-------
CHAPTER 3
SILVER BAY STUDY
August 26, 1965
-------
STUDY OBJECTIVES
The August 26, 1965 water sampling survey conducted in Silver
Bay was made to provide a preliminary evaluation of:
1. Distribution of wastes discharged from the Alaska Lumber and
Pulp Co., Inc. sulfite mill located on Silver Bay.
2. Quality of the Bay waters, primarily in terms of dissolved
oxygen and pH.
3. Water quality changes in Silver Bay resulting from pulp mill
waste discharges.
33
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BACKGROUND
The physical, chemical and biological characteristics of Silver
Bay and approaches near Sitka, Alaska, were the subject of a
comprehensive field survey in 1956-57 conducted jointly by Alaska
Water Pollution Control Board and University of Washington, Department
of Oceanography. The purpose of the survey was to establish existing
environmental conditions and evaluate probable effects of waste
discharge from a planned pulp mill to be located on Silver Bay
(Figure 3-1)'. The study included evaluation of pulp mill wastes and
processes, bioassays to determine biological effects of pulp mill
wastes on marine life, and collection of data on the spatial and
seasonal variations in the physical, chemical, and biological aspects
of Silver Bay waters, shoreline, and bottom.
Alaska Water Pollution Control Board published the study results
and recommendations in their Report No. 10, "Silver Bay Water Pollution
Control Studies" (6). This report, referred to herein as Report No. 10,
contains comprehensive descriptions of the area and its fisheries
resources; pulping processes and waste characteristics; toxic effects
*
of pulp mill wastes on marine life; pre-pollution evaluation of marine
life and water quality in Silver Bay; physical characteristics of the
Bay-area waters including currents, salinities, temperatures, and fresh-
water inflow; and, based on the foregoing, recommendations concerning
waste outfall location and the expected resulting waste distribution
and water quality patterns in Silver Bay. In addition, Report No. 10
^Figures follow page 46
34
-------
recommended a water quality surveillance program to be instituted
following pulp mill construction.
Portions of Report No.10 will be referenced frequently in
presenting and discussing results of the present survey.
The pulp mill, a magnesium-base sulfite process plant, was
subsequently constructed at Sawmill Cove by the Alaska Lumber and
Pulp Co., Inc. and discharges its wastes into surface waters of Silver
Bay near Pt. Bucko (Figure 3-1). In keeping with recommendations of
Report No. 10 for a surveillance program following pulp mill
construction, the State of Alaska, Department of Public Health,
requested this office to conduct the studies reported herein.
35
-------
STUDIES
Water samples were collected on August 26, 1965 at thirteen
stations located in Silver Bay (Figure 3-1). Station locations and
numbering coincide with the thirteen principal sampling stations
occupied during the 1956-57 pre-pollution studies. The sampling period
in relation to predicted tide at Sitka is shown also on Figure 3-1.
Samples were collected from the surface and the 2, 5, 10, 20, 40,
60, and 80 meter depths, depth permitting, at each of the thirteen
stations. Water characteristics determined for each depth were
salinity, temperature, density, dissolved oxygen concentration, pH, and
sulfite waste liquor (SWL) concentration. In addition, total water
depth, surface water clarity, the continuous temperature-depth profile,
and weather were observed for each station.
METHODS
All sampling was conducted from the 45-foot oceanographic research
vessel, HAROLD W. STREETER. Station positioning of vessel was
accomplished using sextant and radar navigation. Water samples at
each station were collected simultaneously with 1.25-liter teflon-
coated Nansen bottles. Each Nansen bottle sampler was equipped with a
reversing thermometer which recorded in _situ water temperature at the
time of sampling. A bathythermograph attached to the lower end of the
hydrographic wire was used to obtain a continuous record of the
temperature-depth profile at each station.
36
-------
Dissolved oxygen concentration, in terms of percent saturation,
and pH were determined in the vessel laboratory immediately after
sample retrieval. Analytical methods were essentially the same as those
employed in the Gastineau Channel studies (see Chapter 1). A 400-ml
portion of each sample was draughted and stored for subsequent salinity
and SWL analyses at Washington Pollution Control Commission laboratory
in Olympia, Washington, as follows:
Salinity -- Salinity in parts per thousand was determined using a
Hytech, Model 6201, inductive salinometer.
SWL -- Sulfite waste liquor concentration in parts per million
by volume was determined using the modified Pearl-Benson
test (7). This test spectrophotometrically measures
the lignin-sulfonate concentration of the sample relative
to a laboratory reference solution of calcium-base, 1070
dry solids by weight, sulfite waste liquor.
Surface water clarity was measured at each station using a 30-cm
diameter, white Secchi disc suspended from a line graduated in meters.
The Secchi-disc reading is a relative measure of turbidity and color
and it represents the maximum depth to which the disc can be submerged
before being obscured from surface view.
All station and sample data thus obtained were processed by
electronic computer at University of Washington data processing center
in Seattle, Washington. Processing provided calculation of water
density and dissolved oxygen percent saturation, and data tabulation.
All data are on file at Federal Water Pollution Control
Administration office, Portland, Oregon.
37
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RESULTS
All data collected during the August 26, 1965 water sampling
survey in Silver Bay have been reduced and tabulated according to
station and depth, and are included in this report in the Appendix.
Based on these data, vertical distributions of SWL, dissolved oxygen
and pH for each of the thirteen sampling stations are presented on
Figures 3-2 through 3-4.
PHYSICAL CONDITIONS DURING SAMPLING PERIOD
Physical conditions in Silver Bay—density stratification, tides,
wind, weather--will affect the distribution of pulp mill wastes and
the resulting water quality. Weather conditions on August 26, 1965
were mild, with light and variable westerly winds less than 10 knots,
overcast skies and intermittent rain. Based on official marine radio
weather reports monitored each day by the HAROLD W. STREETER, weather
throughout this area was very mild for the several days preceding
sampling. Water sampling was conducted during the first part of the
ebb tide (Figure 3-1).
Specific data were not obtained for freshwater inflow to Silver
Bay during the survey period. However, the summer season is normally
a period of higher runoff for the area (see Report No. 10) and
freshwater inflows were probably above average during the August 26
survey. Near-surface salinities within Silver Bay were lower than
those at the entrance, thus indicating a significant amount of
38
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freshwater inflow to the Bay. Based on data in the Appendix, vertical
distributions of salinity and density (in terms of specific gravity) are
shown on Figure 3-5 for a mid-bay transect extending through Stations
1, 3, 6, 11, and 13. This figure illustrates the shallow layer of
lower salinity, lighter density water at the surface resulting from
freshwater inflow. The stability of this layer, due to its
relatively lighter density, inhibits vertical mixing of the surface
waters (and wastes discharged to surface waters) into the deeper Bay
waters.
WASTE DISTRIBUTION
Distribution of pulp mill wastes, as described by SWL concentra-
tions, was widespread in the surface waters of Silver Bay and approaches.
Examination of the station curves (Figures 3-2 through 3-4), the
Appendix, and the salinity-density transect (Figure 3-5) indicates:
1. Wastes are confined to the low-density near-surface layer.
2. Maximum SWL value at each station is at the surface.
3. SWL concentration decreases rapidly with depth at all
stations. Virtually all SWL is situated within 10 meters
of the surface, and most of it is above the 2 meter depth.
Horizontal distributions of SWL in Silver Bay at the surface and
the 2 and 5 meter depths are shown on Figures 3-6 through 3-8.
Surface SWL concentrations vary from a maximum of 3,220 ppm near the
waste outfall at Pt. Bucko to 71 ppm at Station 11. There is no strong
one-way dispersal pattern away from the source which might be related
to a dominant net transport process, .£•£«. strong net outflow of fresher
surface water. Rather, surface SWL distribution is characterized by
39
-------
its widespread uniformity of high concentrations, generally above
200 ppm, throughout the Silver Bay area. This indicates a slow flushing
process with dispersal dominated by tidal action.
WATER QUALITY
Dissolved Oxygen. Based on dissolved oxygen values illustrated
on the station curves (Figures 3-2 through 3-4) and listed in the
Appendix, vertical distribution of dissolved oxygen concentration at
each of the thirteen sampling stations in Silver Bay is characterized
by:
1. Low surface DO concentration; surface values ranged between
49% and 71% saturation (4.4-7.1 mg/1).
2. Rapid increase in DO concentration with depth, from a low
surface value, to a maximum value at a depth between 2 and 10
meters; maximum values ranged from 79% to 90% saturation
(7.2-8.0 mg/1).
3. Gradual decrease in DO concentration with depth below the
depth of maximum concentration; for stations sampled at the
60 meter depth, concentrations ranged from 40% to 62%
saturation (3.9-5.8 mg/1).
Depth of the oxygen-depressed surface layer coincides with the depth
of the waste-confining, low-density layer of fresher surface waters.
Horizontal distribution of dissolved oxygen concentration at
the surface and 2 meter depth is shown on Figures 3-9 and 3-10,
respectively. In general, surface DO concentration is 2-3 mg/1 less
than that at the 2 meter depth. As with the SWL distributions
(Figures 3-6 through 3-8) horizontal distribution of dissolved oxygen
40
-------
at a given depth is quite uniform throughout the Bay area. The
isolated, slightly higher surface-DO value observed at Station 9
(Figure 3-9) is probably associated with freshwater discharge from
Sawmill Creek, as evidenced by the correspondingly low surface
salinity measured at this station (see Appendix).
pH. Vertical distribution of pH at each station (Figures 3-2
through 3-4) is similar to that for dissolved oxygen; _i.£., low
surface value, rapid increase with depth below the surface to a
maximum value at a depth between 2 and 10 meters, and gradual
decrease with depth below the depth of maximum pH. Surface pH values
varied between 7.05-7.65 while those at the 2 meter depth varied
between 7.88 and 8.08. Near-surface lowering of pH occurs in the low-
density surface waters.
Secchi disc. Secchi-disc measurements, shown for all stations
on Figure 3-11, varied from 1.3 to 8.3 meters. Lowest Secchi-disc
readings, jL..e., least transparent waters, were found nearest the pulp
mill where highly colored wastes are discharged. Surface waters
throughout Silver Bay and approaches were observed to have a blackish
cast. In lowering the Secchi disc into the water, the disc was
usually observed to nearly disappear within the first one or two meters
of submergence, then continue to be only faintly visible for another
several meters. This pattern reflects confinement of wastes within
the low-density surface layer.
41
-------
DISCUSSION
Water quality patterns observed in Silver Bay on August 26, 1965
were considerably different than any monitored during the 1956-57
pre-pollution studies , particularly in the waste-confining surface
waters. However, because of the many natural processes which variably
effect DO, pH, water clarity, etc., a specific portion of the observed
change cannot be attributed solely to the presence of pulp mill wastes
on the basis of a single cruise.
In the discussion that follows, SWL and DO values measured on
August 26, 1965 are compared with predicted values outlined in
Report No. 10. In addition, certain apparent effects of pulp mill
wastes on the water quality parameters are described as based on
the present sampling survey.
WASTE DISTRIBUTION
The SWL distribution observed during the August 26 survey did not
closely resemble any of the three patterns predicted in Report No. 10.
The primary differences arise from the basic assumptions for
prediction; (a) that wastes would be uniformly mixed to a depth of
16 feet (about 5 meters), and (b) that transport and dispersal from
the source would be either eastward into the Bay or westward out of the
Bay, depending on the combination of wind, tide, and runoff. Waste
distribution observed on August 26 was not vertically well mixed and
did not exhibit a strong one-way pattern of dispersal away from the
source. Depth-averaging of observed values to a depth of 5 meters
42
-------
would result in values less than one-third of those observed at the
surface. Such depth-averaged values generally would fall within
maximum values predicted at any point (Report No. 10).
It is important to note that wastes are not well mixed and, as
a result, extremely high SWL values occur in surface waters throughout
the Silver Bay area (Figure 3-6). According to bioassay studies
presented in Report No. 10, these observed SWL levels would be more
than sufficient to cause some kill of important food chain organisms
such as copepods, enphausids, mysids, and candlefish. Conditions
prevailing during the August 26 survey were not particularly conducive
to detention of wastes in Silver Bay, and it is expected that even
higher surface SWL concentrations would result during periods of
persistent strong southerly or westerly winds. An increase of SWL
concentration to 500-600 ppm would result in death of herring and
fingerling salmon (Report No. 10). Furthermore, recent bioassay
studies conducted by this office to determine effects of pulp mill
wastes on oyster larvae and bottom-fish eggs show that these immature
life-stages incur severe developmental abnormalities and mortalities
at SWL levels well below those observed in Silver Bay during the
August 26 survey.
WATER QUALITY
Dissolved Oxygen. Distribution of DO in Silver Bay during the
August 26 survey (Figures 3-9 and 3-10) also differed from those
patterns predicted in Report No. 10, primarily in the same respects
as mentioned for the SWL distribution; .i.j:., the presence of vertical
43
-------
concentration gradient near the surface and lack of a strong one-way
dispersal of wastes away from the source. The predicted DO values
(Report No. 10) represent the minimum expected DO values corresponding
to predicted SWL patterns. Depth-averaging of observed DO values to a
depth of 5 meters (16 feet), to compare with predicted values, would
result in average DO concentrations of about 6.5-7.5 mg/1, which is
slightly greater than the predicted minimum values.
Based on the 1956-57 pre-pollution surveys, the summer dissolved
oxygen profile in Silver Bay, in the absence of pulp mill wastes, was
typified by lowest concentration near the bottom, but not less than
6 mg/1, followed by a gradual concentration increase toward the surface
to maximum values of at least 9 mg/1. Also, near-surface waters were
normally supersaturated with dissolved oxygen to at least 5 meters
depth. This increase in DO toward the surface is partially associated
with primary plankton productivity in the presence of sunlight. DO
profiles measured in Silver Bay on August 26 (Figures 3-2 through 3-4),
however, show two significant departures from pre-pollution profiles:
1. DO concentrations below the 60 meter depth throughout the
study area were less than 6 mg/1 and, at Stations 2, 7, and
12, were less than 4 mg/1.
2. Maximum DO values of about 7 to 8 mg/1 (90% saturation or less)
occurred at 2 to 10 meters depth, with a subsequent rapid
decrease toward the surface to low surface values generally
between 4 and 6 mg/1.
It is pointed out in Report No. 10 that any decrease in near-
bottom DO to less than 5 mg/1, over a protracted period (3 or 4 months),
44
-------
would be evidence of decomposition over and above that found
naturally in the Bay. However, up-welled oxygen-deficient ocean water
is normally present at depth by late summer in many of the coastal bays
and inlets along the north Pacific coast. On August 26, DO values less
than 5 mg/1 occurred at depths below 60 meters at the entrance to
Silver Bay (Station 1) in the absence of any detectable SWL while, at
any given depth below 40 meters, DO values within the Bay were generally
less than at the entrance. This suggests that both up-welling and
oxygen utilization in the Bay are responsible for the observed extreme
oxygen deficit at depth.
Examination of the station curves (Figures 3-2 through 3-4) and
the data tabulation in the Appendix shows that the near-surface decrease
in dissolved oxygen is limited to the waste-confining, low-density
surface layer. In this layer, dissolved oxygen concentration
consistently decreases as the SWL concentration increases. This
mirror-image effect is noticeable in areas of Puget Sound, Washington,
where pulp mill wastes also are discharged into estuarine waters.
The near-surface oxygen deficit is attributed to both biochemical
oxygen demand of the pulp mill wastes and to a possible reduction in
phytoplankton oxygen production because of the inhibiting effects of
strong wastes.
The gradual decrease in dissolved oxygen concentration with depth
in the deeper waters is natural but, although decomposition at depth
within the Bay may contribute to this decrease, a specific portion of
the deficit cannot be assigned either to natural causes or to waste
decomposition on the basis of a single cruise. On the other hand,
45
-------
no significant near-surface decrease in DO was observed at any time
during the pre-pollution study; therefore, that observed on August 26
is considered primarily the result of the oxygen demand of pulp mill
waste discharge into Silver Bay. The observed surface DO values
throughtout the area (Figure 3-9) are borderline to the generally
recommended minimum value of 5 mg/1 necessary for marine life and are
less than the 6 mg/1 recommended in Report No. 10 as desirable to
maintain, the fishery at its full potential. In view of the season,
weather conditions, and evident oxygen resource beneath the waste
layer, conditions prevailing during the August 26 survey cannot be
considered the most critical likely to be encountered. Any reduction
of dissolved oxygen beyond that observed on August 26 in the surface
waters of Silver Bay will definitely place the values below recommended
minimum levels.
pH. The pH measured in Silver Bay during pre-pollution studies varied
between 7.2 and 8.4 and, at any given station, generally increased from
a low value at depth to a maximum near the surface. Such a vertical
trend is normal in coastal waters during the summer and is associated
with a relative decrease in dissolved C02 toward the surface. The
COo gradient, in turn, is affected by photosynthetic activity (decreased
C02> increased pH), biorespiration and decomposition (increased CO^,
decreased pH) and dilution by local runoff (generally lower pH). The
pH measured during the August 26, 1965 sampling survey varied from
7.05 to 8.08 and, at each station, increased gradually from a low value
at the bottom to a maximum value at 2-10 meters depth, then rapidly
decreased to a low surface value. The near-surface decrease in pH
46
-------
occurred in the waste-confining, low-density surface waters. No similar
near-surface pH decrease in the presence of low surface salinities was
observed during pre-pollution studies and, for this reason, the lower-
ing of surface pH observed throughout Silver Bay on August 26 cannot
be solely attributed to simple dilution by local runoff. In view of
the waste distribution and dissolved oxygen profile at each station
(Figures 3-2 through 3-4), much of the near-surface decrease in pH
appears to be the combined result of biochemical waste decomposition,
acid nature of the pulp mill wastes, and reduced photosynthetic
production in the waste layer.
47
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TIME IN HOURS
(Pacific StondardTime)
IQOO I20O I4OO 160O 18OO 2OOO
SAMPLING
PERIOD
Predicted tide at Sitka
FIGURE 3-1. Silver Bay study area, sampling locations, and sampling period, August 26, 1965,
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oxygen (DO) and pH at Stations 10-13 in Silver Bay; August 26, 1965.
-------
NAUTICAL MILES FROM STATION NO.I
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specific gravity) along a mid-bay transect in Silver Bay; August 26, 1965.
-------
FIGURE 3-6. Surface concentrations (ppm) of sulfite waste liquor in Silver Bay; August 26, 1965.
-------
FIGURE 3-7. Concentrations (ppm) of sulfite waste liquor at 2 meters depth in Silver Bay; August 26, 1965.
-------
FIGURE 3-8. Concentrations (ppm) of sulfite waste liquor at 5 meters depth in Silver Bay; August 26, 1965,
-------
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-------
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FIGURE 3-10. Concentrations (mg/1) of dissolved oxygen at 2 meters depth in Silver Bay; August 26, 1965,
-------
3-11. Secchi-disc measurements (meters) in Silver Bay; August 26, 1965
-------
CHAPTER 4
WARD COVE STUDY
August 28. 1965
-------
STUDY OBJECTIVES
The August 28, 1965 water sampling survey conducted in Ward
Cove and adjacent waters of Tongass Narrows was made to provide a
preliminary evaluation of:
1. Distribution of wastes from the Ketchikan Pulp Company
pulp mill located on Ward Cove.
2. Quality of the waste-receiving waters, primarily in terms
of dissolved oxygen and pH.
3. Water quality changes in Ward Cove resulting from pulp mill
waste discharges.
48
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BACKGROUND
A comprehensive study of Ward Cove area waters, near Ketchikan,
Alaska, was conducted over a one-year period in 1951-52 by the Alaska
Water Pollution Control Board. Purpose of the study was to describe
chemical, biological, physical, and hydrologic characteristics of
Cove waters prior to construction of a proposed pulp mill to be
located on Ward Cove (Figure 4-1)*
Study results were summarized in Alaska Water Pollution Control
Board Report No. 7, "Ward Cove Survey, Ketchikan, Alaska" (8). This
report, referred to herein as Report No. 7, presents brief descriptions
of the area and its water resources; the annual cycles of dissolved
oxygen concentration and water temperature at selected depths; the
annual cycles of depth-averaged BOD, chlorides, total solids, and
turbidity; ranges and variations of pH, alkalinity, calcium, sulphates,
magnesium, and color; the biological inhabitants of the area waters,
bottom, and shoreline, including the annual cycles of diatoms, copepods,
bottom specimens, and coliform density; and hydrologic data including
freshwater inflow and tidal currents.
Portions of Report No. 7 will be referenced frequently in
presenting and discussing results of the present survey.
Ketchikan Pulp Company, Ketchikan, Alaska, constructed a pulp mill
on Ward Cove in 1954 and since that time has discharged its wastes
into Cove surface waters (Figure 4-2). In order to evaluate the present
condition of Cove waters under this waste loading, the State of Alaska,
^Figures follow page 61
49
-------
Department of Public Health, asked the assistance of this office in
observing waste distribution and water quality in the Ward Cove area.
DESCRIPTION OF THE WASTE SOURCE
The Ketchikan Pulp Company mill operated on Ward Cove is a
magnesi'um-base, sulfite process pulp mill. Production of dissolving
grade pulp is normally about 580 tons/day. Usual recovery operations
are employed to collect, evaporate, and burn the pulping liquor for
recovery of magnesium oxide and return of chemicals to the pulping
cycle.
During the period October 21-24, 1963 this office, in cooperation
with mill management and the Department of Health and Welfare, State
of Alaska, conducted a three-day in-plant survey of mill wastes
discharged from separate unit processes, and as discharged to Ward Cove.
The several in-plant waste streams measured and sampled provided
information concerning waste loads from separate steps in the process.
All wastes from the mill combine to discharge to Ward Cove through two
outfalls which were sampled and measured to obtain data regarding total
plant loading to the waterway. Samples were transported by air-freight
for analysis by the Columbia Basin Project Laboratory of the U. S.
Public Health Service in Portland.
Mill management provided complete information concerning waste
flow and production values. These data, coupled with the analytical
information obtained, permitted calculation of mill losses and waste
loadings to the waterway. Consideration of the values obtained
results in several general conclusions concerning mill wastes discharged
over the survey period as follows:
50
-------
1. The pounds of BOD5 discharged per ton of production was
about 300 pounds on a two-day average with normal recovery operations.
This discharge Level represents a 70% reduction in oxygen demand
loading as compared to BODs values discharged by other Pacific
Northwest mills producing similar products but without recovery and
re-cycle of chemicals.
2. Discharge of sulfite waste liquor solids, as determined by the
Pearl-Benson test, was about 1,100 tons per day or about 3,500 pounds
per ton of product. These values indicate a reduction of about 90%
in materials reactive to this measurement as compared with sulfite
mills without recovery processes.
3. Volatile suspended solids losses were higher than desirable.
The average loss of 88 pounds per ton of product representing 27.7 tons
of volatile suspended solids per day was higher than expected. Volatile
suspended solids losses ranged from 4.2% to 4.5% of production.
Mill wastes are discharged into Ward Cove via two outfalls: the
main sewer, located as shown on Figure 4-2, which discharges about 95%
of the BOD and SWL loadings and over 80% of the volatile suspended
solids; and the woodroom sewer, which handles the remainder of the
wastes, derived mainly from barking operations and magnesium-oxide
recovery process. Based on the in-plant survey, main sewer discharge
averaged 34.4 mgd (about 53 cfs) with the following waste concentrations:
5-day BOD 61° ""g/1
COD (chemical oxygen demand) 1,940 mg/1
Sulfite waste liquor - 7,285 mg/1
Suspended volatile solids 160 mg/1
W Pearl-Benson Index (FBI), calculated on a 10% solids basis.
(see Chapter 3, Page 37 for definition)
51
-------
Mill production during the period of survey averaged 628 tons
per day, somewhat in excess of the designed rate of 580 tons/day.
For this reason mill losses measured may not be truly typical of a
mill operating at design production levels.
52
-------
STUDIES
Water samples were collected on August 28, 1965, at thirteen
stations located in Ward Cove and Tongass Narrows (Figure 4-2).
The sampling period in relation to predicted tide at Ketchikan also
is shown on this figure.
Samples were collected from the surface and the 2, 5, 10, 20,
40, and 60 meter depths, depth permitting, at most of the thirteen
stations, with some minor variation necessitated by limiting depth.
METHODS
Sampling and analytical methods used during the Ward Cove survey
were essentially the same as those used in the previously described
Silver Bay study (see Chapter 3).
All data is on file at Federal Water Pollution Control
Administration office, Portland, Oregon.
53
-------
RESULTS
All data collected during the August 28, 1965 water sampling
survey in the Ward Cove area have been reduced and tabulated
according to station and depth, and are included in the Appendix of
this report. Based on these data, vertical distributions of SWL,
dissolved oxygen and pH for each of the thirteen sampling stations
are shown on Figures 4-3 and 4-4.
PHYSICAL CONDITIONS DURING SAMPLING PERIOD.
Weather conditions on August 28, 1965 were mild, with light
and variable westerly winds less than 9 knots, mostly clear skies and
sunshine. Marine radio weather reports monitored each day aboard the
HAROLD W. STREETER indicated the weather had been mild for several days
preceding sampling.
Samples were collected over a three-hour period beginning near
the time of predicted low tide at Ketchikan (Figure 4-2).
Data concerning freshwater inflow to Ward Cove were not obtained
for the survey. Based on hydrologic information in Report No. 7, local
inflow is primarily from rainfall and, in view of the season and mild
weather, was probably below average during the August 28 study.
Examination of the salinity and density (sigma-t) data in the Appendix
shows:
1. Waters in Tongass Narrows and Ward Cove were stably stratified,
i..e_., density increases significantly with depth at all
54
-------
stations, thus inhibiting downward mixing of surface-
discharged wastes.
2. Near-surface salinity within the Cove is generally less than
that in Tongass Narrows. This indicates at least some local
freshwater inflow to the Cove with a consequent net outflow
in the surface waters.
WASTE DISTRIBUTION
Pulp mill waste, described in terms of SWL, was found in varying
concentrations at all stations sampled (Figures 4-3 and 4-4 and
tabulated data in the Appendix). At each station, maximum SWL value
occurred at or near the surface and ranged from 24 ppm at Station 4 in
Tongass Narrows to 989 ppm at Station 6 in Ward Cove. SWL concentration
decreased rapidly with depth at each station to minimum values of
essentially zero (background in the absence of pulp mill waste) at
depths below 20 meters.
Surface SWL values ranged from 24-41 ppm in Tongass Narrows and
from 485-989 ppm in Ward Cove (Figure 4-5). There was no apparent
strong path of waste movement away from the mill in Ward Cove or away
from Ward Cove in Tongass Narrows.
WATER QUALITY
•
Dissolved Oxygen. Vertical distribution of dissolved oxygen at
each station (Figures 4-3 and 4-4 and tabulated data in the Appendix)
is characterized by:
1. A maximum dissolved oxygen concentration located between
5 and 10 meters depth. Maximum values varied from 7,33 mg/1
55
-------
(85% saturation) in Tongass Narrows to 5.59 mg/1
(64% saturation) in Ward Cove.
2. Decrease in DO toward the surface from the depth of
maximum value. Surface values ranged between 6.41 mg/1
(75% saturation) in Tongass Narrows and 1.76 mg/1
(21% saturation) in Ward Cove.
3. Decrease in DO with depth below the depth of maximum value.
At those stations sampled at 40 meters depth, DO ranged from
4.51 mg/1 (47% saturation) in Tongass Narrows to 1.96 mg/1
(20% saturation) in Ward Cove.
Dissolved oxygen concentration at the 10 meter depth (approximate
depth of maximum DO) was fairly uniform throughout the study area,
varying between about 5.6 and 7.1 mg/1. At any given depth much above
or below the 10 meter depth, DO in Ward Cove was considerably less
than in Tongass Narrows. This latter feature is illustrated on
Figure 4-6 which shows surface DO values in Ward Cove generally
4-5 mg/1 less than those in Tongass Narrows.
£H. Vertical distribution of pH (Figures 4-3 and 4-4 and
tabulated data in the Appendix) essentially followed the same pattern
as for dissolved oxygen concentration, i.£.s maximum values generally
between 5 and 10 meters depth with variable decrease toward the surface
and toward the bottom from the depth of maximum value. Maximum pH for
all stations ranged from about 7.9 to 8.1. Surface pH, shown on
Figure 4-7, varied from low values of about 7.0 in Ward Cove to high
values of about 8.0 in Tongass Narrows.
56
-------
Secchi disc. Secchi-disc measurements, shown for all stations on
Figure 4-8, varied from 0.3 to 1.2 meters in Ward Cove and from 2.6 to
4.6 meters in Tongass Narrows.
57
-------
DISCUSSION
Water quality data collected during the 1951-52 pre-pollution
studies are described in Report No. 7 primarily in terms of values
representative of Ward Cove as a whole rather than as specific values
for a particular time, location, and depth. In the discussion that
follows, water quality observed on August 28, 1965 will be generally
compared with those representative values in Report No. 7, and certain
apparent effects of wastes on water quality will be described on the
basis of the present survey.
WASTE DISTRIBUTION
Review of the surface SWL pattern (Figure 4-5) and the station
curves (Figures 4-3 and 4-4) show two general areas of pulp mill waste
influence: Ward Cove, represented by sampling Stations 6 and 8-13,
where surface SWL ranges between 485 and 989 ppm; and Tongass Narrows,
represented by sampling Stations 1-5 and 7, where surface SWL ranges
between 24 and 41 ppm. The extremely high SWL concentrations throughout
Ward Cove surface waters (485-989 ppm) are well above known toxicity
threshholds for salmon fingerling, herring, candlefish, euphausids,
copepods and mysids (6). Preliminary results of bioassays by this
office in connection with pulp mill pollution in Puget Sound show that
near-surface SWL concentrations in Ward Cove also considerably exceed
values resulting in 100% mortality of egg and larvae stages of oysters
and certain bottom fish, as well as in reduced oxygen production by
58
-------
phytoplankton. The Puget Sound studies also indicate that harmful
effects to the marine environment occur at the lesser waste
concentrations observed in Tongass Narrows (24-41 ppm). Physical
conditions during the August 28 survey were not particularly
contributory to detention of wastes in Ward Cove and, thus, such high
SWL concentrations probably prevail in Ward Cove most of the time.
WATER QUALITY
Dissolved Oxygen. Examination of the surface DO pattern
(Figure 3-6) and the station curves (Figures 4-3 and 4-4) indicates
that the dissolved oxygen regime is separable into the same two areas
as for SWL: Ward Cove (Stations 6 and 8-13 ), where surface DO ranges
from 1.76-2.45 mg/1; and Tongass Narrows (Stations 1-5 and 7), where
surface DO ranges from 6.41-7.24 mg/1. The DO regime is further
divided into (a) near-surface waters above the depth of maximum DO
(generally to about 10 meters depth) where DO decreases toward the
surface as SWL increases, and (b) near-bottom waters beneath the depth
of maximum DO where DO decreases with depth in the absence of strong
SWL.
The envelope of DO versus depth in Ward Cove on August 28,
formed by compositing the DO profiles measured at Stations 6 and 8-13,
is shown on Figure 4-9. In addition, Figure 4-9 shows the DO profile
at Station 4 in Tongass Narrows, a late-summer DO profile representative
of Ward Cove prior to pollution (from Report No. 7), and the recommended
minimum DO value of 5 mg/1. Review of this figure and the station
curves (Figures 4-3 and 4-4) indicates:
1. Near-surface decrease in DO results from presence of pulp mill
59
-------
wastes, the greater the SWL concentration—the less the DO.
2. Near-bottom decrease in DO in the absence of strong SWL,
while expected as a natural characteristic, intensifies with
nearness to the pulp mill, and is considerably more pronounced
in Ward Cove than at more remote stations in Tongass Narrows.
This feature results primarily from high oxygen demands of
settleable solids in the pulp-mill waste discharge (about
1,100 tons per day, page 51) and consequent sludge beds within
Ward Cove. During the August 28 survey, chunks of floating
sludge material, buoyed from bottom deposits by gases of
decomposition, were observed at the inner end of Ward Cove.
3. DO profile at Station 4, the station apparently least
affected by pulp mill wastes (lowest SWL, highest DO) is from
1.2-2.5 mg/1 less than the pre-pollution profile. Some
portion of this difference may be attributable to natural
processes, but the suppressing effect of SWL on near-surface
DO at Station 4 is also noticeable.
4. The DO profile in Ward Cove on August 28, represented on
Figure 4-9 by the composite envelope of all DO values
measured within the Cove, is considerably degraded from that
measured on that day at Station 4 in Tongass Narrows; the
degradation ranges from 4.7-5.5 mg/1 at the surface,
0.6-1.6 mg/1 at 10 meters depth, and 1.0-2.5 mg/1 at
40 meters depth. All of this degradation is attributed to
waste discharge into Ward Cove, i.e., through the combined
effects of effluent and sludge bed BOD and the inhibiting
60
-------
effect of pulp mill waste on oxygen-producing phytoplankton.
5. DO throughout Ward Cove (envelope, Figure 4-9) is less than
the recommended minimum value of 5 mg/1 at depths less than
2-5 meters and greater than 15-19 meters. Preliminary
results of bioassays conducted in Puget Sound by this office
indicate that the presence of SWL and consequent lowered pH
may compound the lethal effect of low DO on fingerling
salmon.
In view of the season and evident oxygen resource beneath the SWL
in Tongass Narrows (at about 10 meters depth), dissolved oxygen
conditions observed on August 28, 1965 do not represent the most
critical likely to occur during the year. The most critical period
would probably be a month or two later, say October, when water
temperatures are still fairly warm but photosynthetic production of
dissolved oxygen is much reduced.
pH. The pattern of surface pH (Figure 4-7) also is divided into
the same two areas as for SWL distribution: Ward Cove (Stations 6
and 8-13), where surface pH ranges from 6.94 to 7.12 in the presence
of strong SWL (485-989 ppm); and Tongass Narrows (Stations 1-5 and 7),
where surface pH ranges from 7.86 to 8.02 at lesser SWL concentrations
(24-41 ppm). The relationship between surface pH and surface SWL,
from low pH at high SWL to high pH at low SWL, is well-defined by the
thirteen stations in Ward Cove and Tongass Narrows, and results from
the combined effects of low pH effluent diluted into the surface waters
and the relative excess of C02 from biochemical waste decomposition
and reduced photosynthesis.
61
-------
FIGURE 4-1. Location chart of the Ward Cove-Tongass Narrows area, near Ketchikan, Alaska.
-------
4
•
A
P T r u 11/ A ki J
: n g • r
toit i
r
&•
2
\ V
X
Predicted tide at Ketchikon
PACIFIC STANDARD TIME
IGURE 4-2. Ward Cove study area, sampling locations and sampling period;
August 28, 1965.
-------
PH
DOlmg/l)
SWUppm)
CO
UJ
5 20
I 3°
H
CL
uj 40
Q
50
PH
D0lmg/|)
SWUppm)
cc I0
UJ
uj 20
5
2 30
Q.
UJ
Q 50
60
PH
DOtmg/l)
SWLtppm)
cc
UJ 10
UJ
20
£ Ml
Q.
UJ
o
STA.1
7 8
Sta.3
> 7
3 4 5 6 7 ' 8
0 10 20 30 ^O 50
6 7 8
O 40 - c» « ~~
I Sta.5 . ,
,ct-P liauor (SWL), dissolved
PTpiTOT-i i c „ ,1 -P-I+-P waste ii-4w(jj- N ' * OQ
oiv 4"3* Vertical distributions °f suUite area; August 28,
°^§en (D) and H at stations 1-5 and 7 in Ward Cove
1965.
-------
PH
DOlmg/l)
SWL(ppm)
0
o:
UJ
t- 10
UJ
•s.
z 20
^ 30
Q.
UI
0 40
1
0
1
-
—
— 1
-
6
2345
200 40O 600 800
I"'"
*~"^**=^
^^^ *\
c VA/ | '
.^s /
•
00^7
/
/ Sta
7
6
1000
1
— <§^
-
f
>
/^
f 1
pH
6
8
7
1
'•o
•
^•-
Y
o
6 78
I 23456 7
0 200 400 600 800 1000
I I 1 I I I '
Sra.8
H
PH
ng/l
SWUppm)
in
cc
UJ
H
UJ
•5.
Q.
UJ
o
20
30
40
PH
D0(mg/0
Q: 10
ui
S 20
30
~
1
0
6 7
23456
200 400 600 800 IOOO
I I I I
Sta.9
8
7
6 7
I 2 3456
0 EOO 400 600 800 IOOO
III'1
8
7
6 7 B
I 234567
0 200 400 600 800 tOOO
, I I I ' ' '
*-
Q-
•>
\
•
X
/^
••o.
o
'
O "
WL
/
Sta.10
Sta.12
pH
D0(mg/l)
SWUppm)
10
20
6 7 8
234567
200 400 600 800 1000
Sfa.13
FIGURE A-4. Vertical distributions of
Oxygen (DO) and pH at Stations 6 and 8-
v 1965.
-------
24
41
. . o
41
881
Z5'
SEE!"
INSET!
r
•
31
989*
.vJ
43 30
so"
485.
875 •
534»
839*
.688
34
4-5. Surface concentrations (PP.) of »»"•"""
study area; August 28, o.
*"
-------
I3I0|45
•
724
SEE
INSET
98l|
ZO '
(3\
55°
6.41
•
,6.47
1.91
1.84*
2.55*
76»
2.45
2.06
$£*
\\
6.57
•
03
6.41
l.79»
FIGURE 4-6. Surface concentrations <*/!) of «»ol«* oxygen in Ward Cove
study area; August 28,
-------
3/10 Nautical MM*
'IGURE 4-7. Surface pH in Ward Cove study area; August 28, 1965,
-------
24'
•
4.6
55°
24'
I
/
11 K A N * 1
1.0*
0.3»
1.0
0.9
•
0.8
FIGURE 4-8 Secchi-disc measurements (meters) in Ward Cove study are
August 28, 1965.
-------
DISSOLVED OXYGEN CONCENTRATION IN MG/L
l/>
ce
UJ
H
UJ
Q.
UJ
O
0
10
20
30
/ 2 3 4 5 6 7
fi i / rmmmm^^^m
" ""-^— -^.
^
—
1 .**"-'
I — — - -^f"' ^ j
1 Envelope of all DO values /
1 measured in Ward Cove /
1 (Stas.6,8-13) ; /
1 Aug. 28, 1965 ™ ~ /
t •'' ' ' •-/
1 -.•••'/ /
\ / /
1 / /
i i
!
'-•-, !
\ v /
'N > J
/ __/ ,/
^X 5/a. no. 4 in
» Tongass Narrows /
/ Aug. 28, 196 5 /
//
.
/ /
/ (
/ 1
' 1
1
1
|
1
Dcrr\kAKAC MPicr\ 1
8 9
i I
\
/
/ Ward Cove
/ Sept. 9, 1952
i (report no. 7)
/
r
MINIMUM D. 0.
50
FIGURE 4-9. Vertical distribution of dissolved oxygen in Ward Cove and at Station 4 in
Tongass-Narrows on August 28, 1965, and in Ward Cove on September 9, 1952.
-------
LITERATURE CITED
AND
APPENDIX
-------
LITERATURE CITED
1 • U. S. Geological Survey. 1962. Surface water records of
Alaska. U. S. Geological Survey, Juneau, Alaska.
2- A.P.H.A. 1962. Standard methods for the examination of water
and wastewater, llth Ed. Amer. Publ. Health Assoc., New York.
626 p.
3- U. S. Coast and Geodetic Survey. 1965. Tide tables, 1965,
West Coast North and South America. U. S. Government Printing
Office, Washington, D. C.
** • U. S. Coast and Geodetic Survey. 1965. Tidal current tables,
1965, Pacific Coast of North America and Asia. U. S. Government
Printing Office, Washington, D. C.
5' U. S. Geological Survey. 1963. Gastineau Channel Study—
administrative report. U. S. Geological Survey, Juneau, Alaska.
6- Eldridge, E. F. and R. 0. Sylvester. 1957. Silver Bay Water
Pollution Control Studies. Alaska Water Pollution Control Board,
Report No. 10. 121 p.
7- Barnes, C. A., E. E. Collias, V. F. Felicetta, 0. Goldschmid,
B. F. Hrutfiord, A. Livingstone, J. L. McCarthy, G. L. Toombs,
M- Waldichuk, and R. Westley. 1963. A standardized Pearl-Benson,
or nitroso, method recommended for estimation of spent sulfite
liquor or sulfite waste liquor concentration in waters.
Tappi 46(6): 347-351.
8- Alaska Water Pollution Control Board. 1953. Ward Cove Survey.
Alaska Water Pollution Control Board, Report No. 7. 21 p.
62
-------
APPENDIX
All data collected during the Silver Bay and Ward Cove field
studies are summarized herein. Data for each of the two survey
areas are arranged by station and depth. A brief explanation of
the data summary format follows:
CRUISE
STATION
DATE
HOUR
ZN
LAT
LONG
WATER DEPTH
WIND DIR
SPD
AIR TEMP
SEC
Self-explanatory
Time zone 8 denotes Pacific Standard
Time.
North latitude of station location
in degrees - minutes - seconds.
West longitude of station location
in degrees - minutes - seconds.
Total depth at station in meters.
Wind direction in degrees referenced
to true north.
Wind speed in knots.
Air temperature in degrees Fahrenheit.
Secchi-disc measurement in meters.
DEPTH
TEMP
SALINITY
SIGMA-T
Sample depth in meters.
In situ water temperature in degrees
centigrade.
Sample salinity in parts per thousand.
A measure of water density; numerically,
sigma-t = (Specific Gravity - 1) 1000.
63
-------
OXYGEN Dissolved oxygen concentration in
terms of milligram-atoms per liter,
milligrams per liter, and percent
saturation,
pH Measure of hydrogen-ion concentration.
SWL Sulfite waste liquor concentration in
parts per million as determined by
the Pearl-Benson test (6).
64
-------
CRUISE SILVER BAY
DATE os/26/65 HR 1400 ZN 03 LAT
WATER DEPTH 141 M WIND DIR 298 SPD
1 STATION 01
DEPTH
o
2
5
10
20
4O
60
80
TEMP,
1 1 ,80
10*05
9.62
9,08
8,07
7,01
5.97
5.90
SALINITY SIGMA-T
28,598
31.655
31.914
32*069
32.139
32 ,?16
32.267
32.391
21.60
24.36
24,63
24.84
25.04
25.25
25.42
25.53
57-01-17 N LONG 135-18-1
>4 AIR TEMP. 60 SEC. 7.
MG-AT,
0.344
0.502
0.464
O.443
0.396
0.369
0.31 1
0.298
OXYGEN
MG/L
5.51
8.03
7.43
7,08
6.33
5,91
4.97
4*76
SATN.
63
90
8?
78
68
62
51
49
PH
7.62
8.08
8.06
7,99
7.96
7.91
7.61
7*57
W
M
SWL
149
8
2
2
0
0
0
o
CRUISE SILVER BAY 1 STATION 0?
DATE 08/26/65 HR 1431 ZN 08 LAT 57-01-55 N LONG 135-14-54 W
WATER DEPTH 73 M WIND DIR 298 SPD 03 AIR TEMP. 60 SEC. 2*8 M
DEPTH
TEMP. SALINITY SIGMA-T
OXYGFN
MG-AT. MG/L SATN.
PH
SWL
0
2
5
10
20
4O
60
12*68
1 O.36
9.70
8.72
7.95
6.51
5.70
27.268
31 *?84
31 .779
31 .995
32.034
32.123
32.222
20.51
24.02
24,51
24.83
24.98
25.24
25,42
0,316
0.435
0.484
0.472
O.448
0,362
0,244
5,05
6,96
7,74
7.55
7.16
5.79
3.91
58
78
86
82
77
60
40
7.65
7.92
7.99
8,05
7,86
7,68
7,54
441
139
12
3
0
0
0
CRUISE SILVER BAY
PATE oe/26/65 HR 1453 ZN 08 LAT
WATER DEPTH 113 M WIND DIR 298 SPD
DEPTH TEMP. SALINITY SIGMA-T
1 STATION 03
57-01-47 N LONG
04 AIR TEMP. 60
135-14-42
SEC. 3.7
W
M
OXYGEN
MG-AT. MG/L SATN.
PH
SWL
0
2
5
10
20
4O
60
80
12.84
10.45
9.66
8.88
7.99
6.48
5,71
5.70
24,267
31 .272
31 .663
31.980
32.061
32. 123
32.232
32.508
18.17
23.99
24,43
24,80
24,99
25,25
25,43
25,64
0.340
0.439
0.449
0.449
0.41 1
0,347
0,268
0.264
5.44
7.03
7.18
7.19
6.58
5.55
4.28
4.23
61
79
80
78
70
57
43
43
7.38
7.96
8.02
7.97
7.90
7.82
7.43
7.58
311
26
15
3
1
1
1
1
-------
CRUISE SILVER BAY 1 STATION O4
DATE 08/26/65 HR 15O9 ZN 08 LAT
WATER DEPTH 37 M WIND DIR 298 SPD
DEPTH
SALINITY SIGMA-T
57-01-39 N LONG 135-14-34 W
04 AIR TEMP* 60 SEC. 5.2 M
OXYGEN PH SWL
MG-AT. MG/L SATN.
0
2
5
10
20
40
12*99
10»64
9.15
8.79
7.81
6.55
23.361
27,026
31 .786
31 .991
32.077
32.143
17.44
20.67
24.60
24.82
25,03
25.25
0.374
0.450
0.438
0.432
0.404
0.338
5.98
7.20
7.01
6.91
6.47
5.41
68
79
77
75
69
56
7.61
8.01
8.03
8.00
7.86
7.72
239
128
7
1
0
0
CRUISE SILVER RAY 1
DATE 08/26/65 HR 1524 ZN 08 LAT
WATER DEPTH 64 M WIND DIR 298 SPD
DEPTH TEMP. SALINITY SIGMA-T
STATION 05
0
2
5
10
20
40
12.44
9.94
9.13
8.57
7.55
6.43
22.390
31.485
31.717
31.980
32.034
32.127
16.79
24,24
24.55
24,84
25.03
25.26
57-02-26 N LONG 135-13-52
06 AIR TEMP. 60 SEC. !•-
MG-AT.
0.336
0.470
0.436
0.405
0.368
0.320
OXYGEN
MG/L
5.38
7.52
6.97
6.48
5.88
5,12
SATN.
60
84
76
70
62
53
PH
7.05
8.02
7.96
7.83
7.67
7.56
W
M
SWL
3220
137
43
4
2
1
CRUISE SILVER BAY
PATE os/26/65 HR 1540 ZN os LAT
WATER DEPTH 64 M WIND DIR 298 SKU
DEPTH TEMP. SALINITY SlGMA-T
0
2
5
10
20
4o
12.58
10.13
9.25
8.65
7.73
6.35
24.118
31 .454
31.752
31.964
32.057
32.104
18.10
24,19
24,56
25.03
25.25
1 STAT
57-02-1
06 AIR
MG-AT.
0.379
0.474
0.443
0.423
0.420
0.338
ION 06
S N LONG
TEMP. 60
135-13-40
SEC. 3.4
W
M
OXYGEN PH
MG/L SATN.
6.07
7.58
7.08
6.77
6.72
5.41
68
85
78
73
71
56
7.64
8.03
7.96
7.91
7.82
7.67
SWL
144
27
27
2
2
1
-------
CRUISE SILVER BAY i STATION 07
0
2
5
10
an
40
60
DEPTH
HR
73 M
1552
WIND
ZN
DIP
08
298
LAT
SPD
TEMP* SALINITY SIGMA-T
13,73
1 0.47
9.10
s,6i
7,86
6,46
5,80
20.650
31,296
31,833
31,968
32,065
32,127
32,240
15.23
24,01
24,65
24,83
25,01
25,25
25,42
57-02-08 N LONG 135-13-29 W
10 AIR TEMP, 60 SEC, 6,2 M
OXYGEN
MG-AT. MG/L SATN,
0,321
0,444
0.451
0,419
0,4O6
0,334
0,245
5,14
7,10
7,22
6,70
6,50
5,34
3,92
58
80
79
73
69
55
40
PH
7,41
8,02
7.96
7,90
7,84
7.70
7,44
SWL
213
22
3
2
0
WATPr-,
*ATER
°EPTH
CRUISE SILVER BAY 1 STATION 08
HR 1611 ZN 08 LAT
DEPTH 40 M WIND DIP 298 SPD
TEMP. SALINITY SIGMA-T
0
2
5
In
30
1 1.79
10.17
9.10
7.78
6.96
26.478
31 .450
31.566
31.864
31.980
32.O38
20,05
24.18
24,44
24,66
24,96
25,12
57-02-44 N LONG
10 AIR TEMP. 60
135-13-32 W
SEC, 2.5 M
c * TM
MG-AT, MG/L SATN,
0,307
0,476
0,431
0.398
0.351
0,329
4,91
7*61
6,90
6,36
5,62
5,26
55
85
75
70
60
55
7.50
8,02
8.00
7.91
7.75
7.63
SWL
308
15
1 1
2
1
1
CRUISE SILVER BAY 1
—. HR 1626 ZN 08 LAT
DEPTH 63 M
0
2
5
10
an
TEMP.
10.18
1 0,47
9.42
8.67
7.73
6.41
5,90
WIND DIR 298 SPD
SALINITY SIGMA-T
15.150
31 .392
31 .597
31
32,007
32,0flt
32, 147
11*54
24«08
24,41
24.77
24.99
2^.2?
25,34
STATION 09
57-02-35
04 AIR
N LONG
TEMP. 59
135-13-10 W
SEC. 2.8 M
OXYGEN
MG-AT. MG/L SATN,
0.441
0.484
0.461
0.426
0
o
,393
,3! 9
7.05
7,74
7,38
6,81
6,28
5,1 1
4,7!
71
87
81
74
67
52
4R
PH
7,50
7,97
7,98
7,99
7.86
7.56
SWL
281
16
12
2
1
1
2
-------
CRUISE SILVER BAY 1 STATION 10
DATE 08/26/65 HR 1441 ZN 08 LAT 57-02*02 N LONG 135-11-53 W
WATER DEPTH 78 M WIND DIR 298 SPD 04 AIR TEMP, 59 SEC» 8,3 M
DEPTH
TEMP,
SALINITY SIGMA-T
OXYGEN PH SWL
MG-AT. MG/L SATN,
0
2
5
10
20
40
60
12,84
10,36
9,12
8.50
7*50
6*24
5.50
18.800
31 .485
31 .705
31 ,941
32.01 1
32.046
32.143
13,96
24. 17
24.55
24,82
25.02
25,22
25,38
0.586
0,475
0,444
O.4O4
0.389
0.336
0,265
5,78
7.60
7,10
6.46
6.23
5.38
4.24
61
85
78
70
66
55
43
7.34
8.08
7.99
7.97
7.85
7.68
7.49
195
11
5
2
1
1
1
CRUISE SILVER BAY 1 STATION 11
DATE 08/26/65 HR 1659 ZN 08 LAT 57-01-55 N LONG 135-12-07 W
WATER DEPTH 82 M WIND f>IR 298 SPD O2 AIR TEMP. 60 SEC. 7.0 M
DEPTH
TEMP.
SALINITY SIGMA-T
OXYGEN
MG-AT. MG/L SATN.
PH
0
2
5
10
20
40
60
13.96
10.19
9.39
8.58
7.52
6.33
5.90
18.950
31*616
31.729
31 .895
32*018
32.069
32.182
13.88
24*30
24,52
24,78
25,03
25,22
25,36
0,319
0,482
0*450
0.418
O.384
0.324
0.256
5,10
7*71
7.20
6.68
6.15
5.19
4.09
57
87
79
72
65
53
42
7.22
8.04
8.03
7.90
7.79
7.57
7.38
SWL
71
6
3
2
2
1
1
CRUISE SILVER BAY 1 STATION
DATE 08/26/65 HR 1715 ZN 08 LAT
WATER DEPTH 91 M WIND DIR 298 SPD
57-01-50 N LONG
02 AIR TEMP. 60
135-12-17 W
SEC. 5.0 M
DEPTH
TEMP,
SALINITY SIGMA-T
OXYGEN PH
MG-AT. MG/L SATN.
SWL
O
2
5
10
20
40
60
80
14,21
10,32
9,38
8.68
7*60
6.32
5.80
5.83
20.500
31.358
31.717
31.930
32*030
32.077
32.213
32.156
15,03
24.08
24,51
24.79
25»02
25.23
25.40
25.51
0.272
0.459
0.439
0.415
0.387
0.323
0.246
0.231
4,35
7.34
7.02
6.64
6.19
5*16
3.93
3.7O
49
82
77
72
66
53
40
38
7.13
7.92
7.92
7.84
7.74
7.49
7.28
7.28
284
22
5
3
1
1
1
0
-------
CRUISE SILVER BAY 1 STATION 13
DATE 08/26/65 HR 1742 ZN OB LAT 57-00-37 N LONG 135-10-05 W
WATER DEPTH 64 M WIND DIR 298 SPD 05 AIR TEMP. 60 SEC* 5*5 M
DEPTH
TEMP.
SALINITY SIGMA-T
OXYGEN PH SWL
MG-AT, MG/L SATN.
n
2
5
10
20
4O
60
14,35
10*03
9.12
8*11
7,14
5.93
^••w 0 •>•••»
21,300
31 .253
31 ,535
31 ,85?
31 ,895
31 .953
31 .984
15,61
24. O5
24,41
24,81
24,98
25.18
— ,
0.285
0.473
0.463
0.442
0.395
0.382
0.361
4.56
7.56
7,40
7,07
6,3?
6,11
5.77
52
84
81
76
66
62
—
7.08
7.88
7.87
7,61
7.50
7.38
7.33
268
24
13
2
2
2
3
-------
CRUISE WARD COVE 1 STATION 1
DATE 08/28/65 MR 0811 ZN 8 LAT 55-32-38 N LONG 131-44-08 W
WATER DEPTH 43 M WIND DIR 345 SPD 07 AIR TEMP. 60 SEC* 3.6 M
DEPTH
TEMP,
SALINITY SIGMA-T
OXYGEN PH
MG-AT. MG/L SATN,
0
2
5
10
20
30
40
13*00
12.88
12.69
9.80
7.81
8.1 i
7*31
27.966
27.970
28.152
30.206
31 ,485
31 ,837
32,182
20,98
21,01
21.19
23.27
24,57
24,80
25*18
0.417
0.428
0.458
0.374
0.312
0.294
0.274
6.67
6.84
7.33
5.99
4.99
4.70
4,38
78
79
85
66
53
50
46
8.01
8.00
8.03
7.88
7.78
7.69
7.60
SWL
26
25
15
3
0
1
1
CRUISE WARD COVE 1 STATION 02
DATE 08/28/65 HR 0824 ZN 8 LAT 55-23-22 N LONG 131-45-09 W
WATER DEPTH 54 M WIND DIR 345 SPD 09 AIR TEMP. 60 SEC. 3.8 M
DEPTH
TEMP*
SALINITY SIGMA-T
OXYGEN PH
MG-AT. MG/L SATN.
0
2
5
10
20
40
50
13.30
13.04
12,88
10.59
8.22
6.70
6.49
27.920
27.920
28.034
29.879
31 .206
32.236
32.473
20.89
20.94
21.06
22.89
24.36
25.31
25*52
0.411
0.413
0.451
0.381
0.327
0.273
0.261
6.57
6.60
7.21
6.10
5*23
4.37
4.17
77
77
84
68
56
45
43
7.95
7.90
7.97
7.85
7.70
7.56
7.48
SWL
34
33
21
4
3
1
1
CRUISE WARD COVE 1 STATION 03
DATE 08/28/65 HR 0846 ZN 8 LAT 55-23-48 N LONG 131-46-32 W
WATER DEPTH 60 M WIND DIR 345 SPD 09 AIR TEMP. 60 SEC. 2.6 M
DEPTH
TEMP.
SALINITY SIGMA-T
OXYGEN PH
MG-AT. MG/L SATN.
0
2
5
10
20
4O
50
13.50
13.09
12.95
1 1 .59
8.72
7.12
6.94
27*860
27.856
28.O61
28.655
31,068
31 .94«=5
32.100
20*81
20,88
21,07
21*77
24,1 1
25,02
25. 17
0.401
0.403
0,438
0,445
0,333
0.288
0.268
6.41
6.45
7.01
7,1?
5,33
4,61
4,28
75
75
81
81
58
48
45
7.87
7.79
7.93
7.93
7.67
7.58
7.51
SWL
41
42
24
12
0
1
-------
CRUISE WARD COVE 1 STATION 04
DATE 08/28/65 HR O9O5 ZN 8 LAT 55-24-57 N LONG 131-47-10 W
WATER DEPTH 64 M WIND DIR 345 SPD Ol AIR TEMP. 60 SEC. 4.6 M
DEPTH
TEMP,
SALINITY StGMA-T
OXYGEN PH
MG-AT. MG/L SATN.
o
2
5
10
20
40
60
13*60
13.33
13.16
12.39
9.30
6*91
6.55
28.13ft
28.126
28.168
28.514
30.683
32.069
32.411
21 .OO
21 .05
21.1 1
21.52
23.72
25.15
25.46
0.453
ft. 453
O.454
0.446
0.352
0.282
0.273
7.24
7.25
7*27
7.14
5.63
4.51
4.37
85
85
85
82
61
47
45
8.02
7.95
7.95
7.96
7.79
7.64
7.54
SWL
24
23
22
10
2
0
CRUISE WARD COVE 1 STATION 05
DATE 08/28/65 HR 0920 ZN 8 LAT 55-23-57 N LONG 131-46-00 W
WATER DEPTH 29 M WIND DIR 298 SPD 09 AIR TEMP. 60 SEC. 4.5 M
DEPTH
TEMP.
SALINITY SIGMA-T
OXYGEN
MG-AT. MG/L SATN.
PH
O
2
5
10
13.50
13.09
13.07
12.34
27.958
27.962
28.000
28.335
20.88
20.96
21 .00
21 .39
O.404
0.401
0.4O7
0.428
6.47
6.42
6.51
6.85
76
75
76
79
7.86
7.80
7.84
7.87
SWL
41
40
36
22
20
9.20
30.667
23.72
0.352 5.63
61
7.69
CRUISE WARD COVE 1 STATION 06
DATE 08/28/65 HR 0935 ZN 8 LAT 55-23-41 N LONG 131-44-06 W
WATER DEPTH 47 M WIND DIR 298 SPD 09 AIR TEMP. 60 SEC. 1.0 M
DEPTH
TEMP. SALINITY SIGMA-T
OXYGEN PH SWL
MG-AT. MG/L SATN.
0
2
5
10
20
40
13.46
13.23
12.90
12.01
8.42
6.85
25.706
26.916
27.598
28.629
31.079
32.123
19.16
20.13
20.72
21.68
24.16
25.20
0.112
0.220
O.308
0.349
0.308
0.219
1.79
3.52
4.92
5.59
4,92
3.51
21
41
57
64
53
37
6.94
7.15
7.52
8.08
7.83
7.72
989
507
254
16
1
1
-------
CRUISE WARD COVE 1 STATION 07
DATE 08/28/65 HR 0952 ZN 8 LAT 55-23-50 N LONG 13t-44-20 W
WATER DEPTH 49 M WIND DIR SPD 00 AIR TEMP. 60 SEC. 4.2 M
DEPTH
TEMP.
SALINITY S1GMA-T
OXYGEN PH
MG-AT. MG/L SATN.
o
2
5
10
20
40
13.41
13.16
13.08
12.32
8.46
6.83
28.0O8
28.015
28*015
28.442
31.106
32.147
20.94
20.99
21.01
21.48
24,18
25.22
0.401
0.409
0.409
0.4O9
0 . 296
0.215
6.41
6.55
6.55
6.55
4.73
3.44
75
76
76
75
51
36
8.00
8*07
8.04
8.03
7*85
7.62
SWL
31
32
32
17
0
CRUISE WARD COVE 1 STATION 08
DATE 08/28/65 HR 10O5 ZN 8 LAT 55-23-56 N LONG 131-43-37 W
WATER DEPTH 42 M WIND DIR SPD 00 AIR TEMP. 60 SEC. 0.9 M
DEPTH
TEMP,
SALINITY SIGMA-T
OXYGEN PH
MG-AT. MG/L SATN.
SWL
O
2
5
10
20
40
14.21
13.37
12.99
12.02
8.75
6.87
26.067
27.496
28.617
28.617
30.971
32.01 1
19.29
20.55
21.49
21.67
24.03
25.1 1
0.129
0.283
0.380
0.391
0.295
0.123
2.06
4.52
6.08
6.26
4.72
1.96
24
53
71
72
51
20
7*i i
7.68
7.97
8*03
7*88
7.40
650
166
17
17
1
2
DATE 08/28/65 HR
WATER DEPTH 44 M
CRUISE WARD COVE 1 STATION 09
1018 ZN 8 LAT 55-24-03 N LONG 131-43-48 W
WIND DIR 254 SPD 04 AIR TEMP. 66 SEC. 1.2 M
DEPTH
TEMP.
SALINITY SIGMA-T
OXYGEN PH
MG-AT. MG/L SATN.
SWL
O
2
5
10
20
40
14.13
13.30
13.08
12.46
8.80
6.89
26.203
27.738
27,927
28.438
30.933
32.088
19.41
20.75
20.94
21.45
23.99
25.17
0.153
0.322
0.371
0.390
0.283
0.149
2.45
5.15
5.94
6.24
4,52
2,39
29*
60
69
72
49
25
7.12
7.84
7.98
8.05
7.80
7.51
688
96
53
21
3
2
-------
DATE 08/28/65 HR
WATER DEPTH 34 M
CRUISE WARD COVE 1 STATION 10
1031 ZN 8 LAT 55-24*08 N LONG 131-43-25 W
WIND OIR 254 SPO 04 AIR TEMP* 66 SEC* 1 ,0 M
DEPTH
TEMP*
SALINITY SIGMA-T
OXYGEN PH SWL
MG-AT. MG/L SATN.
0
2
5
10
20
30
14,56
13*34
12*98
12,21
9*31
7.77
24,464
27.556
27*905
28*206
30*579
31 *485
18,00
20,61
20,94
21,31
23,64
24,57
0,110
0,271
0,360
0,403
0,241
0,178
1,76
4,33
5*76
6*45
3,85
2,85
21
51
67
74
42
30
6,95
7,75
8,00
8,04
7,78
7,55
839
1O4
51
22
3
2
CRUISE WARD COVE 1 STATION 11
DATE 08/28/65 HR
WATER DEPTH 31 M
DEPTH
0
2
5
10
20
30
TEMP.
14*28
13*26
12*99
12*73
9*16
7*79
1043 ZN
WIND DIR
SALINITY
23.831
27.386
27.818
28.194
30.614
31 *504
8 LAT
SPi
SIGMA-T
17.57
20,49
20*87
21*21
23*69
24*58
55-24-13 N LONG 131-43-32 W
) 00 AIR TSMP. 65 SEC. 0.3 M
OXYGEN PH
MG-AT. MG/L SATN.
0.159
0.301
0.362
0.406
0.206
0.141
2.55
4*81
5.79
6*50
3.29
2.26
30
56
67
75
36
24
7.16
7.68
7.88
8.03
7.72
7.53
SWL
534
146
78
24
4
2
CRUISE WARD COVE 1 STATION 12
DATE O8/28/65 HR 1058 ZN 8
WATER DEPTH 21 M WIND DIR
LAT 55-24-18 N LONG 131-43-36 W
SPO 00 AIR TEMP. 65 SEC. 1.0 M
DEPTH
TEMP.
SALINITY SIGMA-T
OXYGEN PH SWL
MG-AT. MG/L SATN,
o
2
4
14
9
19
14,63
13*22
13*06
12*28
12*81
9,02
24,095
27,659
27,814
28*564
28.133
30.756
17,70
20.71
20,86
21.58
21 ,15
23*82
0.115
0.254
0,314
0,378
0,387
0,145
1,84
4,06
5,02
6,05
6,19
2,32
22
47
58
69
72
25
6.94
7*72
7*80
8*04
7*98
7.51
874
91
66
17
26
3
-------
CRUISE WARD COVE 1 STATION 13
DATE 08/28/65 HR 111? ZN 8 LAT 55-24-22 N LONG 131-43-22 W
WATER DEPTH 16 M WIND D!R SPD 00 AIR TEMP. 65 SEC. 0.8 M
DEPTH
TEMP.
SALINITY SIGMA-T
OXYGEN PH SWL
MG-AT. MG/L SATN.
0
2
5
10
14,45
13*53
13,00
12*63
22,516
27.371
27,213
28*?59
16,53
20,43
20,41
21 ,28
0,119
0.222
0.318
0.377
1 *91
3,55
5*10
6*03
22
42
59
70
7.08
7.60
7,81
7,90
485
63
49
24
15
1 1 ,89
28.59B
21 ,67
0*316 5,05
58
7*87
18
------- |