E PA-R 2-72-111
Environmental Protection Technology Series
NOVEMBER 1972
Correlated Studies of
Vancouver Lake - Water Quality
Prediction Study
Office of Research and Monitoring
U.S. Environmental Protection Agency
Washington, D.C. 20460
-------
RESEARCH REPORTING SERIES
Research reports of the Office of Research and
Monitoring, Environmental Protection Agency, have
been grouped into five series. These five broad
categories -were'established to facilitate further
development and application of environmental
technology. Elimination of traditional grouping
was consciously planned to foster technology
transfer and a maximum interface in related
fields. The five series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioeconomic Environmental Studies
This report has been assigned to the ENVIRONMENTAL
PROTECTION TECHNOLOGY series. This series
describes research performed to develop and
demonstrate instrumentation, equipment and
methodology to repair or prevent environmental
degradation from point and non-point sources of
pollution. This work provides the new or improved
technology required for the control and treatment
of pollution sources to meet environmental quality
standards.
-------
EPA-R2-72-111
November 1972
CORRELATED STUDIES OF VANCOUVER LAKE-
WATER QUALITY PREDICTION STUDY
By
Surinder K. Bhagat
William H. Funk
Donald L. Johnstone
Project 16080 ERQ
Project Officer
Dr. Curtis C. Harlin, Jr.
National Water Quality Control Research Program
Robert S. Kerr Water Research Center
Ada, Oklahoma 74820
Prepared for
OFFICE OF RESEARCH AND MONITORING
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
For sale by the Superintendent of Documents, U.S. Government Printing Office, Washington, D.C., 20402 - Price $2
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EPA Review Notice
This report has been reviewed by the Environmental Protection
Agency and approved for publication. Approval does not
signify that the contents necessarily reflect views and
policies of the Environmental Protection Agency, nor does
mention of trade names or commercial products constitute
endorsement or recommendation for use.
11
-------
ABSTRACT
This study deals with the restoration of water quality of shallow,
polluted, and eutrophic lakes. Dredging and removing of lake bottom
sediments and introducing better quality water are the restoration
measures explored in this study. Vancouver Lake, Washington, was
used as a test case.
Hydrologic, hydrographic, hydrodynamic, and water quality information
provided by separate but correlated studies, was combined with the aid
of mathematical simulation models. Dissolved oxygen was used as an
indicator of the overall water quality in the system. Photosynthesis,
atmospheric reaeration, biological respiration, and advection were the
mechanisms considered in the computation of diurnal changes in dissolved
oxygen level. In addition to the DO model, the aquatic life model for
computing time-varying levels of phytoplankton and bacteria was also
tried. The validity of these models was verified with the actual field
data. After verifications of the models under the existing conditions,
they were used to project and predict the water quality of Vancouver
Lake as will be affected by dredged lake depths and introduced flows
from the Columbia River.
This report was submitted in fulfillment of Project Number 16080ERQ
under the partial sponsorship of the Office of Research and Monitoring,
Environmental Protection Agency.
111
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CONTENTS
Section
I
II
III
IV
V
VI
VII
VIII
IX
X
XI
Conclusions
Recommendat ions
Introduction
Sampling and Measurement
Water Quality of the Columbia River
Quality of Vancouver Lake Sediments
Water Quality Prediction Approach
Prediction Results and Discussion
Acknowledgment s
References
Appendices
Page
1
3
5
11
15
59
45
71
79
81
85
-------
FIGURES
PAGE
1 VANCOUVER LAKE - COLUMBIA RIVER SYSTEM 6
2 FLOW CHART OF VANCOUVER LAKE STUDIES 8
3 PONTOON BOAT 12
4 PORTABLE CONTINUOUS WATER QUALITY MONITORING 14
SYSTEM
5 TOTAL COLIFORM DENSITY OF COLUMBIA RIVER AT 22
VANCOUVER, WASHINGTON
6 TOTAL COLIFORM DENSITY OF COLUMBIA RIVER AT 23
VANCOUVER, WASHINGTON
7 FECAL COLIFORMS AND FECAL STREPTOCOCCI DATA 24
OF COLUMBIA RIVER AT VANCOUVER, WASHINGTON
8 FECAL COLIFORMS AND FECAL STREPTOCOCCI DATA 25
OF COLUMBIA RIVER AT VANCOUVER, WASHINGTON
9 TOTAL PLATE COUNT DATA OF COLUMBIA RIVER AT 26
VANCOUVER, WASHINGTON
10 ALGAE OBSERVED IN COLUMBIA RIVER IN DECEMBER, 30
1969
11 ALGAE OBSERVED IN COLUMBIA RIVER IN FEBRUARY, 31
1970
12 ALGAE OBSERVED IN COLUMBIA RIVER IN APRIL, 32
1970
13 ALGAE OBSERVED IN COLUMBIA RIVER IN JUNE, 33
1970
14 ALGAE OBSERVED IN COLUMBIA RIVER IN AUGUST, 34
1970
15 NUTRIENT LEVELS IN COLUMBIA RIVER AT VANCOUVER, 37
WASHINGTON
16 VERTICAL NUTRIENT PROFILE OF VANCOUVER LAKE 40
BOTTOM SEDIMENTS
17 MEAN SEASONAL VARIATIONS IN LAKE DEPTHS .AND 47
NET INFLOW-OUTFLOW RATES OF LAKE RIVER TO
VANCOUVER LAKE FOR EXISTING CONDITIONS
VI
-------
FIGURES
PAGE
18 AVERAGE ANNUAL FLOWS 49
19 RELATIVE CONCENTRATION OF DYE IN VANCOUVER 50
LAKE f-DDEL AS FUNCTION OF TIME
20 LAKE DETENTION TIME AND AVERAGE INFLOW THROUGH 51
ANY KIND OF CONDUIT(S)
21 COMPARISON BETWEEN SIMULATED AND OBSERVED 68
DISSOLVED OXYGEN CONCENTRATION IN VANCOUVER
LAKE
22 COMPARISON BETWEEN SIMULATED AND OBSERVED 69
ALGAL CONCENTRATION IN VANCOUVER LAKE
23 COMPARISON BETWEEN SIMULATED AND OBSERVED 70
TOTAL BACTERIA CONCENTRATION IN VANCOUVER LAKE
24 PREDICTED EFFECTS OF DREDGING AND INTRODUCING 72
COLUMBIA RIVER WATER ON WATER QUALITY IN
VANCOUVER LAKE
25 PREDICTED EFFECTS OF DREDGING AND FLUSHING ON 74
TOTAL ALGAL COUNTS IN VANCOUVER LAKE
26 PREDICTED EFFECTS OF DREDGING AND FLUSHING ON 75
TOTAL BACTERIA COUNT IN VANCOUVER LAKE
27 SENSITIVITY OF DISSOLVED OXYGEN TO PHYTOPLANKTON 77
SPECIFIC GROWTH RATE, y
VI1
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TABLES
No. Page
1 Bacteriological Water Quality of Columbia River 16
at Vancouver - Portland
2 Algae Distribution in the Columbia River 28
3 Summary of Columbia River Water Quality 36
4 Carbon, Nitrogen, and Phosphorus in Vancouver 39
Lake Bottom Sediments
5 Algae Growth Potential of Vancouver Lake Bottom 41
Sediments - Columbia River Water
6 Some Trace Elements in Vancouver Lake - Columbia 42
River System
7 Comparison of Average Water Quality of Vancouver 46
Lake and Columbia River
8 Functional or Estimated Co-efficients for Water 61
Quality Model
9 Water Quality Input Data Used in Water Quality 73
Model for Verification and Prediction
VI11
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SECTION I
CONCLUSIONS
1. Without curtailing the present sources and amounts of pollution to
Vancouver Lake and dredging the lake to provide 15 feet of water,
a flow of about 750 cubic feet per second diverted from the Columbia
River to Vancouver Lake will be required to raise the dissolved
oxygen level in the lake to 8 mg/1. This diverted flow vill also
reduce the amount of pollution that enters the lake via the Lake
River during high tides in the Columbia River.
2. Water quality simulation models are useful tools in studying, pre-
dicting and analyzing complex aquatic systems provided the models
are verified with actual field data. Research is needed to establish
numerical values of various coefficients and to refine the functional
relationships that apply under a variety of environmental conditions.
The accuracy of the models depends upon the accuracy of the values
of coefficients used and the functional relationships assumed.
3. The sensitivity analysis conducted in this study strongly suggests
that the diurnal variations in dissolved oxygen are very sensitive
to the phytoplankton specific growth rates. Furthermore, in matching
the computed values with the actual field data, the effect of_temper-
ature on the values of the specific growth rate could not be ignored
as suggested in the literature. The specific growth rate value of
0.09 per day per degree centigrade best simulated the summer condi-
tions in Vancouver Lake.
4. In verifying the validity of the water quality simulation models,
actual field data should'be available on a continuous basis for at
least the critical periods in water quality.
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SECTION II
RECOMMENDATIONS
It is recommended that the information developed in this study should
be used as guidelines in the initial as \\rell as final stages of modifi-
cations of the Vancouver Lake System. It is further recommended that
the Environmental Protection Agency partially sponsor a study which
would provide continuous monitoring of Vancouver Lake, under the post-
modification period, of such water quality parameters as have been used
in this simulation model study. The purpose of the recommended proposed
study is to check the predicted results and then to make modifications
in the water quality model so that the model can be used bv others in
analyzing other lakes by incorporating the changes corresponding to the
conditions being studied.
-------
SECTION III
INTRODUCTION
This study is one of several related studies conducted on Vancouver
Lake which in its present condition is polluted and therefore is of
limited value to the nearby communities of Vancouver, Washington and
Portland, Oregon. However, this shallow inland body of water has the
potential of becoming a useful multipurpose resource.
Description of the Study Area
Vancouver Lake (Figure 1) lies immediately northwest of the city of
Vancouver, Washington and only four miles across the Columbia River
from Portland, Oregon. The lake is bounded on the northwest, west
and south by a low-lying ground area which separates the lake from
the main channel of the Columbia River. To the east and the north-
east, the lake is bounded by hills on which are located rapidly
expanding residential areas. The lake has an average surface area of
2,600 acres. Except for periods of flooding, Vancouver Lake has an
average depth of only three feet.
The principal inlet streams are Burnt Bridge Creek on the southeastern
end and Lake River on the northern end of the lake. The Burnt Bridge
Creek, containing high pollutional loads, drains from elevated hilly
areas east of the lake where residential development is largely served
with septic tanks. Lake River, which connects the lake with the
Columbia River, reverses its flow direction with the change in the
tides. The lake receives tidal .flows from Lake River during high tides.
Of the several tributaries that discharge into Lake River, Salmon Creek
is the major tributary that receives significant loads of sediments
and nutrients from the agricultural, industrial, and domestic activities
located in its drainage basin. Seasonally, the inlet streams are
heavily loaded with sediment, and organic and inorganic nutrients. The
tidal flats at the north end of Vancouver Lake and the existing poor
water quality are evidences of incoming pollution load.
Previous Studies
Prior to 1965, many agencies and individuals have made limited effort
toward improving the usefulness of this lake through studies and
various projects. A summary of these studies is included elsewhere.
Vancouver Lake, Lake River and the separating lowlands constitute a
13,000 acre complex having 12 miles of Columbia River frontage. This
complex has been and is being studied for recreational, industrial,
agricultural and navigational development. One or more interconnecting
channels between the lake and the Columbia River and dredging of
-------
Lake Riv. and Columbia Riv.
Join near Ridgefield
LEGEND
o Automatic woter
level recorders
A Woter quality
stations
Model outline
Figure 1. Vancouver Lake -- Columbia River System
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Vancouver Lake are being considered as possible methods of increasing
lake use potential and as a water quality improvement measure. A study
dealing with the development plan for the 13,000 acre complex was com-
pleted in September, 1967. (*•) This study was sponsored by the
Washington State Department of Commerce and Economic Development through
a federal grant from the Department of Housing and Urban Development
under the Urban Planning Assistance Grant Program authorized by Section
701 of the Housing Act of 1954, as amended. This study made an attempt
to determine the location and the extent of land that should be assigned
to the various uses of the complex. A wide variety of ideas for
improving the quality of the water-land environment in order to enhance
the usefulness of the area was proposed by this study and by others,
In 1966, the College of Engineering Research Division, Washington State
University (WSU) , was contacted by the Port of Vancouver to determine
possible alternatives for restoring Vancouver Lake. After exploration,
it was found that practically no water quality, hydrologic, hydrographic ,
and related water quantity data were available on Vancouver Lake, Lake
River, or their tributaries. A preliminary proposal, indicating the
need for various correlated studies which would establish a data base
and then consider a broad range of alternative solutions for improving
the quantity and quality of Vancouver Lake, was prepared. Between 1966
and 1969, separate proposals were submitted to the appropriate agencies
and the funds were finally secured to undertake these studies. A flow
chart of Vancouver Lake studies is shown in Figure 2 and a summary of
the studies conducted by WSU is given below:
1. Hydroclimatic Study: *- J This study was sponsored by the Federal
Water Pollution Control Administration and WSU, and it was com-
pleted in May, 1968. The primary purposes of the study were to
determine: (a) the physical, chemical, biological and bacterio-
logical water quality in Vancouver Lake-Lake River System, (b) the
levels of nutrients and the types and populations of living orga-
nisms in the lake bottom sediments, and (c) the sources of pollu-
tion to the system.
2. Hydrologic Study: ^ ^ This study was sponsored by the Port of
Vancouver and WSU, and it was completed in September, 1971. The
main purpose of this study was to determine the amount of water
coming into and leaving Vancouver Lake under existing conditions.
3. Hydrographic Study: ^ ' This study was also sponsored by the Port
of Vancouver and WSU and it was completed in September, 1971. The
purpose of this study was to determine changes in depth and volume
in the lake as a result of variations in inflow and outflow in the
existing system.
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LOCAL & FEDERAL AGENCIES
(CONCEPTUAL & PLANNING STUDIES)
U.S.C.E, EARLIER FLOOD
AND NAVIGATION STUDIES
(ALSO U.S.G.S. DATA)
Circa: 1952. 1966. ...
F.A.I.R, STUDY
Port of Vancouver: 1966
ST&R COMPLEX
DEVELOPMENT PLAN
Port of Vancouver: 1967
CLARK COUNTY
REGIONAL PLANNING
COUNCIL STUDIES
O-
v
CURRENT AND FUTURE
U.S.C.E,FLOOD AND
NAVIGATION STUDIES
COLLEGE OF ENGINEERING
RESEARCH DIVISION
WASHINGTON STATE UNIVERSITY
(BASIC INFORMATION STUDIES)
HYDROCLIMATIC
STUDY
EPA: May, 1968
HYDROGRAPHIC
AND
HYDROLOGIC
STUDIES
Port of Vancouver: 1969-1971
•o
HYDRAULIC MODEL STUDY
EPA: 1969-1971
vy
WATER QUALITY
PREDICTION STUDY
SPA: 1969-1971
FUTURE DESIGN
AND DEVELOPMENT
STUDIES
Figure 2. Flow Chart of Vancouver Lake Studies
-------
4. Hydraulic Model Study:^ •* This study was sponsored by Federal
Water Quality Administration (now the Environmental Protection
Agency) and WSU and it was completed in June, 1972. The main
purpose of this study was to investigate the influence of alter-
nate channel routes from the Columbia River into and out of
Vancouver Lake on the flushing action in the lake, sedimentation
and erosion patterns, detention times, river-lake stage relation-
ships, and other factors which would influence flow into and out
of Vancouver Lake.
Objectives
The purpose of this project was to combine the results of hydroclimatic,
hydrologic, hydrographic, and hydraulic model studies with the quality
of the proposed inflow from the Columbia River and evaluate the water
quality which could be expected in Vancouver Lake. It was the intent
of the project that water quality prediction techniques developed for
Vancouver Lake could be applied to other shallow lakes.
Specific objectives included in this study are:
a. Determination of seasonal variations in water quality in the
Columbia River in the vicinity of Vancouver, Washington,
b. Establishment of seasonal variations in water quality of
Vancouver Lake under the present conditions,
c. Determination of diurnal variations in dissolved oxygen,
temperature, etc. in Vancouver Lake during the critical
conditions which generally occur in the month of August,
d. Determination of variations in nutrient levels in bottom
sediments with sediment core depth, and
e. Development of a mathematical model for prediction of water
quality in Vancouver Lake for the post-development conditions
(dredging of the lake and connecting the south of the lake
with the Columbia River through a channel or culverts).
-------
SECTION IV
SAMPLING AND MEASUREMENTS
The Hydroclimatic Study, ' which was completed in 1968, provided suffi-
cient information on the seasonal variation of water quality in Vancouver
Lake-Lake River System, the sources of pollution to the system, and the
nutrient levels in the top few inches of the lake bottom sediments.
However, additional information was necessary to achieve the objectives
of this project and, hence, sampling and measurements were primarily
directed toward determining the quality of water which might be diverted
from the Columbia River to Vancouver Lake, determining the quality of
the lake sediment core samples, and establishing the diurnal variations
in water quality of Vancouver Lake.
Sampling
After careful study of the possible locations of Columbia River water
diversion to the lake, two water quality sampling stations on the
Columbia River \vere selected. These stations and the continuously
monitoring station in the center of the lake are shown in Figure 1.
Additional water quality stations shown in Figure 1 were used in the
1968 Hydroclimatic Study.
Based on low and high water levels and extreme seasonal changes, five
detailed field water quality surveys of the Columbia River were made
during December 1969, and in 1970 during the months of February, April,
June and August. During each survey, water samples at surface, mid-
depth and near bottom were taken at 1/4, 1/2, and 3/4 river widths at
each station.
A self-propelled pontoon boat (Figure 3) was used for sampling and for
some direct water quality measurements. The boat, having a deck area
of 160 sq. ft., provided sufficient space for six people, storage of
necessary equipment and instruments, and for on-the-spot measurement
and analysis of some water quality parameters. The boat equipment
included pH meters, dissolved oxygen probes and analyzers, thermisters,
a sonar depth measuring instrument, conductivity meters, a VanDorn
water sampler, homemade chemical kits for measuring alkalinity, hard-
ness and dissolved oxygen (Winkler), turbidimeters, portable ice chests,
portable bacteriological incubators, a submarine photometer, bottom
organism sampling and identification equipment, various reagents for
chemical testing and preserving of water and biological samples, a
variety of sample containers and bottles, necessary glassware, bottom
sediment coring equipment, etc.
Initially, the plan was to collect sediment core samples from five
locations (north, south, east, west, and center) in the lake and
three times during the study period. However, because of high water
11
-------
-
Figure 3. Pontoon Boat
12
-------
conditions and the problem with the initial coring device, the exten-
sive sampling of the lake was limited to the month of August in 1970.
Sediment core sampler, which was borrowed from the Pacific Northwest
Water Laboratory at Corvallis (noiv under EPA), did not prove to be
entirely satisfactory for core sampling in Vancouver Lake. The bottom
sediments in Vancouver Lake were rather compacted at places and were
"soft" at other places. The Corvallis core sampler was designed for
sampling soft bottoms. Therefore, a homemade coring device, which
could be driven by hand or by hammering, was constructed. The device
proved adequate for our needs. During the high water levels in the
lake, the core sampling was limited to the shallow areas, and during
the low water levels in August 1970, an extensive sediment core
sampling was achieved.
Measurements
A variety of measurements, which provided information on the bacterio-
logical, limnological, nutrient, and environmental aspects of water
quality, was made during each of the field water quality surveys.
Nearly all of the bacteriological, phytoplankton, physical, and some
of the chemical analyses were made, within 12 hours of sampling, on
the boat or in the nearby borrowed laboratories of Clark College and
Sewage Treatment Plant of Vancouver. For other examinations and
analyses, samples were properly stored and transported to Sanitary
Engineering Laboratories in Pullman which is located about 350 miles
east of Vancouver, Washington.
To acquire data, on a continuous basis, on the diurnal variations in
levels of dissolved oxygen, temperature, pH, and conductivity in the
lake during the critical period (low water levels and high water
temperatures), the following setup was used. A floating wooden plat-
form, 81 x 6', was installed in the center of Vancouver Lake. The
platform was used to house instruments and a recorder which \vere
operated on a continuous basis with rechargeable batteries. The cali-
bration and operation of the system were checked once or twice a week.
The system for monitoring dissolved oxygen, temperature, pH, and
conductivity included a Hydro-lab water quality analyzer \Mhich con-
sisted of five modules, housed in a main frame, for the simultaneous
measurement of up to five water quality parameters, water quality
sensing probes, a marine field scanner, and a strip chart recorder.
The marine field scanner received output of each of the water quality
variables from the main frame and it in turn transmitted this infor-
mation to the strip chart recorder. The monitoring system (Figure 4)
was completely portable.
13
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Figure 4. Portable Continuous Water Quality
Monitoring System, A: sensing
probes; B: main analyzer; C: scanner;
D: strip chart recorder
14
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SECTION V
WATER QUALITY OF THE COLUMBIA RIVER
Bacteriological Quality
The purpose of bacteriological examination of an aquatic environment
has been, in the past and still is to a great extent, to measure the
degree of potential hazard to public health. Public health consider-
ation, beyond any doubt, should remain of high priority. However,
water quality degradation caused by bacteria which do not directly
affect public health but otherwise interfere with the normal uses of
water should also be of concern. The case in point is the presence
of bacteria of the genus Sphaerotilus, which are responsible for slime
growths in streams. These slime growths have been kno\vn(7,8,9)to
collect and clog the nets of fishermen, interfere with fish hatching
by coating fish eggs, and smother aquatic flora and fauna that serve
as food for fish.
Although bacterial water quality standards for most bodies of water in
the U.S. are based on the total'coliform density, it is believed by
many public health bacteriologists that the widely used total coliform
density is not adequate as the sole criteria for protecting public
health. Geldreicht10) states that the fecal coliform density provides
a better basis for protecting the public health during water-contact
activities and that the fecal coliform test for monitoring water
quality is the most accurate available. Measurements must be based
on detection of fecal contamination by all warm-blooded animals. When
fecal coliform densities are above 200 organisms per 100 ml, a sharp
increase in the frequency of Salmonella detection is found in fresh
water and estuarine pollution. According to Geldreich the recommended
limit of 200 fecal coliforms per 100 ml for primary contact recreational
water use is consistent with research findings. The State of Washington
Class A interstate water quality standards state that total coliform
organisms shall not exceed median values of 240 colonies per 100 ml
with less than 20 percent of the samples exceeding 1,000/100 ml when
associated with any fecal source. In accordance with the characteristic
uses for Class A waters, the bacterial standards would permit water
contact sports such as swimming, water skiing, etc., to be carried on
without a hazard to public health.
The bacterial quality of Columbia River (designated as Class A stream)
was assessed by examining the water for total coliforms (TC), fecal
coliforms (FC)', fecal streptococci (FS), plate counts (PC), Sphaerotilus
counts (Sphaer), and pigmented bacteria (Pig). The detailed results
are given in Table 1. The variation of total coliform density, fecal
coliform and fecal streptococci data, and the total plate counts for
the two stations and for the two river widths (total plate count data
plotted only for 1/2 river width) are shown in Figures 5, 6, 7, 8, and
9. The data presented in these figures are averages of bacterial counts
15
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Table 1. Bacteriological Water Quality of
Columbia River at Vancouver - Portland
Sampling
Station
Date
TC
FC
FS
FC/FS
%NFC
PC/ml
Sphaer/ml
Pig/ml
«.
X (D
is n)
C U^
O --i
4-> C O
cti C. rt
4-> 03 <-M
C/J ,£ ?-t
u 3
.1
* S 4J
C PH
O i— 1 C 1
03 C T3
4-> rt -rH
LO >C S
u
£
i — ' *"O Ei
35= -H- O
5= 4->
C 4J
O --H 0
nJ c H
4-1 Cti Oj
C/5 ^ 03
u z:
' l»— t-
Dec.
Feb 4
Apr.
June
Aug.
Dec.
Feb.
Apr.
June
Aug.
Dec.
Feb.
Apr.
June
Aug.
4,
,
7,
12
4,
4,
4,
7,
12
4,
4,
4,
7,
12
4,
1969
1970
1970
, 1970
1970
1969
1970
1970
, ' 1970
1970
1969
1970
1970
, 1970
1970
560
310
-10
20
400
370
340
-40
<10
700
440
110
-10
100
200
90
50
~2
0
36
34
78
<10
0
39
55
18
-3
~3
11
21
17
~3
0
2
10
26
-4
0
5
30
9
-4
-1
1
4.3
2.9
-0.8
0.0
18.0
3.4
3.0
-
0.0
7.8
1.8
2.0
-0.7
-3.0
11.0
84
84
-80
100
91
91
77
-75
-
94
87
83
~70
97
94
96,000
72,000
66,000
33,000
20,700
40,000
71,000
68,000
26,000
45,000
85,000
68,000
44,000
39,000
45,000
-500
-200
*
*
*
*
~60
*
*
*
*
~800
*
*
*
30,000
8,700
22,000
2,600
-6,000
16,400
23,000
35,000
2,500
7,000
22,000
21,000
11,000
1,500
6,000
31
12
33
8
13
41
32
51
10
16
26
31
25
4
13
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Table 1 (cont.). Bacteriological Water Quality of
Columbia River at Vancouver - Portland
Sampling
Station
fi
•H —* T3 E
*fc T-I O
3: P
d j i
O r-l O
• H Q> CQ
P G
rt G H
P oj cti
c/3 X 0>
^
Date
Dec.
Feb.
Apr.
June
Aug.
Dec.
Feb.
Apr.
June
Aug.
Dec.
Feb.
Apr.
June
Aug.
12,
4,
7,
12,
4,
4,
4,
7,
12,
4,
4,
4,
7,
1969
1970
1970
1970
1970
1969
1970
1970
1970
1970
1969
1970
1970
TC
300
~30
<10
<10
800
300
-12
<10
<10
300
400
>9
<10
12, 1970 <10
d,
1970
700
FC
3
13
0
1
8
7
12
0
2
10
5
9
0
1
-
FS
1
7
0
0
2
3
13
-1
2
4
1
7
0
0
1
FC/FS
~3.0
1.8
0.0
~1.0
4.0
2.3
0.9
-
-1.0
2.5
5.0
1.2
-
-
0.0
%NFC
99
56
-
-
99
97
0
-
~80
97
99
0
-
-
100
PC/ml Sphaer/ml
26,000 *
66,000 *
20,600 "10
6,900 *
7,500 ~10
37,000
61,000 *
36,000 *
7,700 *
10,600 *
39,000
70,000 *
20,000 *
8,000 *
10,100 *
Pig/ml
9,500
16,000
7,100
1,500
1,600
9,000
7,000
13,000
2,300
2,100
10,000
14,000
8,000
2,400
1,500
%Pig
36
24
34
20
21
24
11
36
30
20
25
20
40
30
15
-------
Table 1 (cont.). Bacteriological Water Quality of
Columbia River at Vancouver - Portland
00
Sampling
Station
Date
TC
FC
FS
FC/FS
%NFC
PC/ml
Sphaer/ml Pig/ml
%Pig
X O
CM T3 CX
C "~ CO
O •— <
•H (U
-------
Table 1 (cont.). Bacteriological Water Quality of
Columbia River at Vancouver - Portland
Sampling
Station
CH CO
• H O GL)
j_j fij tm
Date
Apr.
June
Aug.
7, 1970
12, 1970
4, 1970
TC
-50
30
5,600
FC
-50
18
268
FS
-40
4
17
FC/FS
~1.2
4.5
15.7
%NFC
0
40
95
PC/ml
125,000
32,000
120,000
Sphaer/ml
~200
*
*
Pig/ml
52,000
2,300
14,000
%Pig
41
7
11
C/5
U
CO
0}
u
Apr. 7, 1970 >70 ~70
June 12, 1970 20 9
Aug. 4, 1970 8,700 280
- 5
0
24
~14.0
-9.0
11.6
0
55
97
97,000
41,000
220,000
-100
-100
*
41,000
5,500
21,000
42
13
9
-------
Table 1 (cont.).
Bacteriological Water Quality of
Columbia River at Vancouver - fbrtland
tSJ
o
S amp ling
Station Date TC FC
FS FC/FS %NFC PC/ml Sphaer/ml Pig/ml
%Pig
X 0>
4-> i-H
* 3 1* Apr. 9, 1970 <10 0
.2 "3 d, June 12, 1970 <10 4
2 | «2 Aug. 4, 1970 700 22
-M P*
CM '"O E
* £ w Apr. 4, 1970 <10 0
•2 'g 8 June 12, 1970 10 0
& jj 3 Au8' 4' 197° 4>200 189
4->
C "~ d,
'2|° Aug. 4, 1970 7,500 192
p^ C *"O
4J S3 ._H
u
to Iri-
0 0.0 - 3,400,000 * 2,680,000
0 -4.0 - 8,000 * 2,300
'4 ~5.5 97 10,900 ~ 100 2,200
0 0.0 - 31,000 * 6,000
1 0.0 -100 16,900 * 4,800
10 18.9 96 65,000 * 10,000
12 16.0 97 82,000 * 4,500
78
29
20
19
28
15
5
-------
Table 1 (cont.)- Bacteriological Water Quality of
Columbia River at Vancouver - Portland
Station8 Date TC FC FS FC/FS %NFC PC/ml Sphaer/ml Pig/ml %Pig
=tfc *H O
3£ +-*
.2 «£ Aus- 4> 197° 3'100 14° ~5 ~28<0 95 41>000
4J C
Pj Ci f-H
+j o3 oi
IV)
3,600
TC = Total Coliforms No./lOOmls
FC = Fecal Coliforms No./lOOmls
FS = Fecal Streptococci No./lOOmls
FC/FS = Ratio of Fecal Coliforms to Fecal Streptococci
%NFC = Percent of Nonfecal Coliforms
PC/ml = Total Count/ml
Sph/ml = Sphaerotilus/ml
Pig/ml = No. Pigmented Bacteria/ml
%Pig = Percent of Pigmented Bacteria
* Below level of detection at 1:10 dilution
- No calculated value
-------
8000
6000
4000
3000
2000
1000
E
O
o
a:
Ld
Cu
CCL
Ld
h-
U
<
QC
U_
O
Od
Ld
CD
"00
20
10
RTTO1 STATION I
(UPSTREAM)
STATION 2
(DOWNSTREAM)
1/4 CHANNEL W.DTH
§
I
S
V
V
s
V
V
by
X
X
v^
DEC.,1969 FEB.,1970 APR.,1970 JUN.,1970 AUG.,1970
FIGURE 5. TOTAL COLIFORM DENSITY OF
COLUMBIA RIVER AT VANCOUVER, WASHINGTON
22
-------
4000
3000
2000
1000
E
O
o
UJ
CL
QC
LJ
I-
o
<
OQ
cr
UJ
OD
100
20
10
STATION I
(UPSTREAM) 1
STATION 2 I
(DOWNSTREAM)
1/2 CHANNEL WIDTH
i;
P
m
i
i
?a
i«
i
1
I
1
I
I
s
&
DEC.,1969 FEB.,1970 APR.,1970 JUN.,1970 AUG.,1970
FIGURE 6. TOTAL COLIFORM DENSITY OF
COLUMBIA RIVER AT VANCOUVER, WASHINGTON
-------
E
O
O
a:
LJ
Q.
tr
UJ
i-
o
<
QQ
o:
UJ
CO
25
20
10
lOOr
I
FECAL
STREPTOCOCCI
g
&x
E
G
t—
iXV5a STA
&MJ STA
TION ll
TION 2f '/4 CHANNE:L WIDTH
^
.
•
-
1
Vs
I
V^!
V
$
vS
i
WJ
1
V
^
s
*v^
(
V
27<
^ *
FECAL
COLIFORM
w***
^
ra te&
m
|:ji
1
YM'/'/'/'A
\
V
1
^V
^
*•***!
1
1
'**"•*
i
Jjjj!
1
p
$&
10-
5 -
DEC.,1969 FEB.,1970 APR.,1970 JUN.,1970 AUG.,1970
FIGURE 7 FECAL COLIFORMS AND FECAL
STREPTOCOCCI DATA OF COLUMBIA RIVER
AT VANCOUVER, WASHINGTON
24
-------
£U
l/"\
If J
1 NX
5
E
0
0
-
-
1
§:•:
***»*'
i
•x*
jXj
$x':
i
¥x
^
i
s
i
FECAL
w
%^5
V
S
1
1
1
^
•&
n
1
STREPTOCOCCI
S
\
38
K:;
$:
'&
&:
*•*•*
&':
.;.«
1
1
iT
cL 200
<
E
[£ 100
o
CD
50
u_
O
o:
Lul
CO
^
*
10
5
i
E
•
^
v55
X
STATION 'I |/2 CHANNEL WIDTH
m STATION 2(
)
^
V
V*
X
1
x'i
1
I
i
:::$
Sft
§
x$
1
X
Cs
1
1
•x'i
a
i
i
:¥:•
:^x
FECAL
COLIFORM
r»*^ (O\
P^P E?X] rrsri ^ X
1
J:§
i
1
•X*
$S
1
:¥:
¥:•;
i
•x«
xc
i
1
#:i
^
DEC.,1969 FEB.,1970 APR.,1970 JUN.,1970 AUG.,1970
FIGURE 8. FECAL COLIFORMS AND FECAL
STREPTOCOCCI DATA OF COLUMBIA RIVER
AT VANCOUVER, WASHINGTON
25
-------
STATION
STATION 21
1/2 CHANNEL WIDTH
2XI05r
o:
LJ
Q_
cr
LJ
H-
O
<
m
u.
O
tr
LJ
CD
103
5X10'
l
8
I
s
I
1
1
1
1
;••%
I
1
FIGURE 9. TOTAL
COLUMBIA RIVER
DEC.,1969 FEB.,1970 APR.,1970 JUN.,1970 AUG.J970
PLATE COUNT DATA OF
AT VANCOUVER, WASHINGTON
26
-------
measured at water surface, mid-depth, and near bottom. Generally, the
bacterial counts at station 2, the downstream station, were higher than
at station 1, the upstream station. Also, the counts were generally
higher in winter months and late summer period than in early summer
months. It appears that the bacterial intensity is inversely propor-
tional to the flow in the Columbia River. The flow of the Columbia
River varies considerably during the year with flow increasing gradually
during March and April, increasing abruptly during May and June, and
decreasing again in July. The flow normally remains low during the
fall and winter months,'although high water can occur during the winter
months.
In examining Figures 5 and 6, it can be seen that the median value for
TC is well within the Class A stream standards. It should be noted,
however, that the TC counts were excessively high during August. The
counts of FC were below 200 organisms per 100 ml in all cases except
in August at 1/4 channel width at station 2 (Figures 7 and 8). Also,
the ratio of FC/FS, in most cases, was greater than 0.6 (Table 1)
indicating that contamination was largely from domestic sewage. Geldreich
et al.CHJ anci Kenner et al. C1ZJ report that the ratio of FC/FS for man
is 4.4 and that for other warm-blooded animals it is 0.6 or less. Table 1
further indicates that, in most cases, the fecal coliforms constituted
less than 30% of the total coliforms. In summary, bacterial quality of
the Columbia River as it exists today should present no health hazard to
the public in its use of the river for water-contact recreation.
Generally, the presence of Sphaerotilus in the Columbia River water was
measurable in winter months and the levels in summer months were
generally below the detectable limit. The significance of 10 to 800
Sphaerotilus organisms per ml that have been detected in our sampling
in the Columbia River has not been determined so far as proposed diver-
sion of river water to Vancouver Lake is concerned.
The chromogenic or pigmented bacteria are comprised of those bacteria
able to form visible pigmented colonies on modified Henrici's agar at
room temperature in 2 days. Chromogenic colonies ranged in color from
light yellow through yellow orange and red orange and from pink to red
with some purple colonies. Preliminary identification placed them in
the genera Flavobacterium, Xanthomonas, Pseudomonas, Brevibacterium,
and Micrococcus.Most of the isolants were gram negative rods.Some
colonies produced a melanin-like diffusible black pigment. The signif-
icance of the organisms is not known at present.
The numbers of chromogenic bacteria are indicative of the overall
quality of surface waters. The populations of chromogenic bacteria
in the Columbia River was.in agreement (Table 1) with the findings of
other investigators. (13'i4»15J Plating media with reduced amounts of
nutrients are in many instances replacing the standard plate count
agar (Standard Methods). Chromogenesis is more evident when the_orga-
nisms are grown on a low nutrient medium. The numbers chromogenic
-------
bacteria usually comprise are about 20 to 40% o£ the total populations
capable of growing on low nutrient media. (14,15,1 j
average 24% of the total colony count with a range of 4 to 781 in
Columbia River waters. Waters of exceptionally high quality (arctic
lakes) may exhibit only 5% of the total population as chromogenic.
During our investigation, a 5% figure was observed only once (Table 1) .
It is desirable in a comprehensive bacteriological survey of surface
waters to enumerate not only the bacteria of sanitary significance
but also to enumerate those indigenous to the stream. The results of
previous studies indicate that total counts,^ in relatively unpolluted
'""3,18,19) Ti^g average tot
streams average 4.0 x 104 bacteria per ml.
The average total
count for Columbia River waters is 6.0 x 10H bacteria/ml (Table 1).
This average is not significantly higher than those of previous inves-
tigations. High quality waters usually exhibit values of approximately
3.0 x 10^ bacteria per ml. ^-9,20) ^he difference in total counts from
station 1 to station 2 can be attributed to urban influences. This
type of impact has been well documented.(13,18) when the higher counts
are considered with respect to the usual numbers encountered in highly
polluted water (1.0 x 10^), their significance is unimportant.(18,21)
Phytoplankton
At each of the two stations on the Columbia River, algae measurements
were made at three equal river widths and at three water depths (surface,
mid-depth, and near bottom) for each river width. The data indicated
no major variations in the species and their numbers with respect to
depth, width, or station but there were definite changes in species and
their numbers with respect to time. These algae data are summarized in
Table 2. It can be seen that the peak algae concentrations occurred in
the month of June when the numbers reached 4,700 cells per ml. In April
and in August the concentration ranged between 1,000 and 2,000 cells per
ml whereas the concentration remained below 300 cells per ml during the
months of December and February.
Table 2. ALGAE DISTRIBUTION IN THE
COLUMBIA RIVER
1969
December
1970
February April June
August
Total cells/ml 256
Diatoms (I) 68.0
Greens (I) 15.2
Blue Greens (%) 0.0
Others (I) 16.8
71.6
14.8
0.0
13.6
1060
84.9
0.0
0.0
15.1
4691
77.0
15.2
0.4
7.4
1682
73.0
11.0
0.7
15.3
28
-------
Table 2 further shows the distribution of algae into the three groups--
diatoms, greens, and blue greens. Diatoms were the predominant algae
present in the Columbia River throughout the year, making up 68 to 851
of total algae. The greens constituted from 0 to 15%, blue greens less
than 1%, and other unidentified species 7 to 17% of the total algae.
The blue greens were observed only in the months of June and August.
Detailed tabulations of the algal species observed in the Columbia
River are given in Appendices A and B. The relative abundance of algal
forms observed in the months of December, February, April, June, and
August are shown in Figures 10,11, 12, 13 and 14, respectively. In
December 1969, the nost prevalent form was Asterionella and other
prominent diatoms were Fragilaria, Melosira, and Stephanodiscus.
Tribonema, belonging to the yellow greens, was the only other identi-
fiable form present. All these forms were also observed in February
1970, but in smaller numbers, and the dominant form was Fragilaria
which increased in numbers and remained dominant by April 1970. At
that time another form, Melosira, was observed and by June this genus
had surpassed other algae and showed a concentration of about 2,000
cells per ml at station 2. Other identified algae observed, in consid-
erable numbers, in the month of June were Fragilaria, Tribonema,
Asterionella, Stephanodiscus, Tabellaria, Scenedesmus, and Oscillatoria.
A decrease in concentration of algae \\ras observed in August 1970 and
the forms identified in decreasing order were Tabellaria, Fragilaria^
Stephanodiscus, Tribonema, Asterionella, Melosira, Scenedesmus, andT"
Oscillatoria.
The fact that 85% of the algae that make up the phytoplankton population
of the Columbia River are diatoms strongly indicates that the water
quality of this stream is presently in good condition. This fact,
coupled with the observation that blue greens make up only about 0.4
to 0.71 of the populations and these occur during the warmer months of
late June through August, is another indication that these waters are
in good condition. It is recognized that some blue greens are present
in waters of excellent condition as well as certain diatoms are present
in polluted waters, but the wide variety of clean water species is
indicative of the overall water conditions. Over 50 different species
of diatoms were represented--25-30 species of greens and only 5 species
of blue greens--which gives an indication as to the variety of phyto-
plankton present. This variety and number of clean water species
present would indicate that the body of water is in a mesotrophic state
of nutrition.
Nutrients and Other Parameters
The detailed data on 5-day biochemical oxygen demand (BOD), chemical
oxygen demand (COD), total solids (TS), total volatile solids (TVS),
suspended solids (SS), volatile suspended solids (VSS), total phosphorus
and soluble phosphorus expressed as P04, organic nitrogen, ammonia
nitrogen, and nitrate nitrogen are given in Appendix C. A summary of
29
-------
ASTERIONELLA
MELOSIRA
KXXl
STEPHANODISCUSema TRIBONEMA mm
FRAGILARIA ^m\ OTHER FORMS
'•
CO
UJ
100
75
50
25
STATION I
Xp'-
1
STATION 2
FIGURE 10. ALGAE OBSERVED IN COLUMBIA RIVER IN DECEMBER,I969
-------
ASTERIONELLA E2ZZZ3
STEPHANOD1SCUS
FRAGILARIA
MELOSIRA
TRIBONEMA
OTHER FORMS
txxxi
30
I , I
20
UJ
CJ
10-
•
1
Xv
STATION I STATION 2
FIGURE ll. ALGAE OBSERVED IN COLUMBIA RIVER IN FEBRUARY, 1970
-------
STEPHANODISCUS
FRAGILARIA
MELOSIRA
OTHER FORMS
200
i
V)
-j
_j
UJ
100
txa
STATION I STATION 2
FIGURE 12. ALGAE OBSERVED IN COLUMBIA RIVER IN APRIL, 1970
-------
'-•
ASTERIONELLA B2ZZ3
SJEPHANODISCUS E22S
FRAGILARIA ETSTSI
1444
J
s
O>
UJ
1100
1000
900
800
700
600
500
400
300
200
100
n
-
-
-
•
•
I
MELOSIRA
TABELLARIA
TRIBONEMA
STATION I
SCENEDESMUS
OSCILLATORIA
OTHER FORMS
1961
STATION 2
FIGURE 13. ALGAE OBSERVED IN COLUMBIA RIVER IN JUNE, 1970
-------
I
-J
IE
ASTERIONELLA USZS&
STEPHANODISCUS
FRAGILARIA
900r
800
700
600
500
Oj 400
o
300
200
100
0
MELOSIRA
TABELLARIA
TRIBONEMA
E2S3 SCENEDESMUS
F^^ OSCILLATORIA
E5D1Q OTHER FORMS
m
STATION I
STATION 2
FIGURE 14. ALGAE OBSERVED IN COLUMBIA RIVER IN AUGUST, 1970
-------
these parameters and also of other water quality parameters such as
alkalinity, pH, hardness, sulfates, Pearl-Benson index (FBI), chlorides,
dissolved oxygen, temperature, and conductivity is presented in Table 3.
The values included in Table 3 are derived for the most part from the
entire data collected at the two stations, three river widths at each
station, and three depths for each river width.
The 5-day BOD values measured were always less than 2.0 mg/1 and the
average was about 1.0 mg/1. The COD values ranged from 2.5 to 14.0
mg/1 with 5.8 mg/1 as the average.
Total nitrogen varied from 0 to 1.38 mg/1 and the average was about
0.35 mg/1 (Table 3). Most of the nitrogen measured was in the forms
of nitrates and organic nitrogen. The nitrate levels gradually increased
from December to April and then there was an abrupt drop from April to
June (Figure 15). The organic nitrogen remained about constant from
December to February and then gradually decreased from February to
June. The ammonia levels stayed about constant during the study period.
The total phosphate levels ranged from 0.04 to 0.85 mg/1 as P04 with an
average value of 0.23 mg/1. On the average, 501 of the phosphorus
measured was in the soluble form and the remaining 501 was associated
with the suspended solids.
Generally, the nitrogen and phosphorus levels were low (Figure 15)
during the summer months when high biological activity was noticed
(Table 2).
The concentration of total solids ranged from 68 to 180 mg/1 with an
average value of 116 mg/1. On the average, about 30% of the total
solids were volatile solids. The concentration of suspended solids
varied from 0 to 35 mg/1 and the average was about 18 mg/1. On the
average, about 33% of the suspended solids were volatile.
The measurements summarized in Table 3 indicate that the water quality
of the Columbia River, at present, is in good condition and the river
can be used for recreational and other purposes. The levels of phos-
phorus are higher than 0.01 mg/1 as P, the border-line level recognized
by some and disputed by others, between eutrophic and non-eutrophic
waters.
35
-------
Table 3. SUMMARY OF COLUMBIA RIVER WATER QUALITY
Concentration, mg/1
BOD
COD
NH3-N
Org-N
N03-N
Total P-P04
Soluble P-P04
TS
TVS
SS
VSS
PH
Alk-CaC03
Hardness-CaC03
S04
PBI
Cl
DO
+Temp .
*Conductivity
Minimum
0
2.5
0
0
0
0.04
0.01
68
18
0
0
7.6
18
18
0
0
2.3
8
4
65
Maximum
2.1
14.0
0.15
0.53
0.70
0.85
0.72
180
64
35
15
8.2
79
78
11
0.52
5.5
12
21
210
Average
1.0
5.8
0.05
0.11
0.19
0.23
0.12
116
34
18
6
8
47
63
6.6
0.1
4.1
9
167
0.
2.
0.
0.
0.
0.
0.
23
9
8
4
20
13
2
0.
1
36
a
44
50
036
072
18
13
11
13
*Conductivity is given in units of y mhos
+Temp. is given in °C
36
-------
0.4
0.3
o>
O.I
0
N03-N
0.4
•*
Q_
Q- O
TOTAL P-P04
SOLUBLE P-P04
o>
_
O
CO
DEC I FEB
1969 x
APR JUN
1970
AUG
FIGURE 15. NUTRIENT LEVELS IN COLUMBIA
RIVER AT VANCOUVER, WASHINGTON
37
-------
SECTION VI
QUALITY OF VANCOUVER LAKE SEDIMENTS
Quality of Vancouver Lake bottom sediments was assessed by measuring the
organic matter, phosphorus, and nitrogen levels in the sediment core
samples collected throughout the lake. Also, the potential of these
sediments to support phytoplankton populations was evaluated on a quali-
tative basis. A few samples were analyzed by the method of neutron
activation analysis to determine the levels of some of the trace elements
available in the lake sediments. Data on bottom organisms as collected
previously(3) are also summarized.
Nutrients
Generally, the nutrient levels in the top six inches of bottom sediments
were higher than in the remaining core. There were some pockets of high
nutrient levels observed even at deeper than six inches of core depth.
Typical vertical profiles of nutrient levels in Vancouver Lake bottom
sediments, as observed in August 1970, are shown in Figure 16. It
should be noted that the ammonia-nitrogen levels increased with core
depth whereas organic nitrogen, phosphorus, COD and volatile solids,
generally, decreased with core depth.
It should also be mentioned that previous findings^ ' indicate that the
levels of nutrients in the top layers of Vancouver Lake bottom sediments
were the highest in the winter months and the lowest in the late summer
period.
The minimum, maximum, and average values of organic carbon, nitrogen,
and phosphorus derived from the 43 Vancouver Lake sediment analyses are
summarized in Table 4. A similar analysis of "sewage sludge in river"
as found by others (22) j_s a^so included in this table for comparison.
It can be seen that the bottom sediments of Vancouver Lake come close
to resembling "sewage sludge in river."
Table 4. CARBON, NITROGEN, AND PHOSPHORUS IN
VANCOUVER LAKE BOTTOM SEDIMENTS
Ratio
%C %N IP C:N N:P
Maximum 2.66 0.31 0.14 20 4
Minimum 0.40 0.05 0.06 4 0.5
Average 2.00 0.20 0.10 10 2
Sewage Sludge 5.8 0.28 0.18 21 2
in River *-22J
39
-------
10
LU
5 15
CL
UJ
Q
.
O
O
20
25
30
COD VS
NH3-N
ORG-N
P-P04
20
FIGURE 16.
40
60
80 0 I 2
CONCENTRATION, mg/g DWB
VERTICAL NUTRIENT PROFILE OF VANCOUVER LAKE
BOTTOM SEDIMENTS
-------
Also, organic sediment index (OSI), which is a product of percent organic
nitrogen and percent carbon measurements of sediments, was computed and
the values of OSI for Vancouver Lake sediments varied from 0.02 to 0.82
with an average value of 0.4. According to the classification suggested
by Ballinger and McKee,(23) ^be Vancouver Lake sediments fall between
type I and type II sediments. The type I sediments represent sand,
clay, and old stable sludge, and the type II sediments represent organic
detritus, pea-t, and partially stabilized sludge.
Laboratory studies *• ' with lake bottom sediments from three lakes in
west-central Minnesota indicated that the sediments can act as reser-
voirs of orthophosphate and that the release of orthophosphates from
the sediment to the water takes place when the phosphate concentration
in the overlying waters is low. In evaluating the nutrient concentra-
tions measured in sediments, it is important to know the nutrient
fraction that is available for biological reactions and the fraction
that is not available. Although the determination as to what fraction
of nutrients in sediments is available for biological activity was not
in the scope of this study, a small qualitative study to gain infor-
mation related to this topic was undertaken. This study involved 25-
250 ml glass flasks, each of which contained five grams of Vancouver
Lake sediment and 100 ml of the Columbia River water, and 3-250 ml glass
flasks, each of which contained 100 ml of the Columbia River water only
to serve as controls. The sediments used in this study were taken from
the five locations (north, south, east, west, and center of the lake)
in Vancouver Lake and from five core depths at each location. The
flasks were exposed to about 300-foot candles fluorescent light intensity
in a room maintained at 20°C. The experiment was continued for seven
weeks, and the results of algae growth observations are summarized in
Table 5.
Table 5. ALGAE GROWTH* POTENTIAL OF VANCOUVER LAKE
BOTTOM SEDIMENTS - COLUMBIA RIVER WATER
„. ^4.1** Sediment Core Depth (inches)
Time Control** ^ ^ J-
(Weeks) 0-5 5-10 10-15 15-20 20-25
0
1
2
3
5
7
NG
NG
NG
'r1
i\\3
NG
NG
NG
NG
SG
SG
AG
AG
NG
NG
NG
NG
SG
SG
NG
NG
NG
NG
SG
SG
NG
NG
NG
NG
LG
SG
NG
NG
NG
NG
LG
LG
*Algae growth observations denoted as: NG - no growth, LG - little
growth, SG - sparse growth, and AG - abundant growth.
**Columbia River water with no Vancouver Lake sediments added.
41
-------
It appears that the nutrients in the top five inches of the lake sedi-
ments were sufficiently "available" to produce abundant algae growth
which took place after the 3rd week and before the 5th week of the
experiment. It can also be concluded from this experiment that the
"availability" of nutrients in sediments at depths greater than about
five inches was scarce.
Trace Elements
Neutron activation analysis technique was used to determine the levels
of some of the trace elements present in the sediments and water. The
results are summarized in Table 6. The levels of nine elements found
in Vancouver Lake sediments are of the same magnitude as present in
average basalt rocks. Cobalt is one of the trace elements that has
been recognized as essential for the growth of blue green algae and it
is required in concentration of 0.5 mg/l.'-25'' It appears from Table 6
that there is no deficiency of cobalt in the Vancouver Lake system.
Table 6. SOME TRACE ELEMENTS IN VANCOUVER LAKE-
COLUMBIA RIVER SYSTEM
Concentration in ppm
Vancouver Lake
Columbia
Element
Iron
Cobalt
Chromium
Barium
Scandium
Europium
Hafnium
Thorium
Rupidium
Sediments
5 x 104
18.5
57.5
500-700
18.5
1.42
7.35
17.10
90.2
Water
ND*
1.02
8.9
ND
0.95
0.06
ND
0.60
ND
Water
ND
0.58
8.9
ND
0.14
0.06
ND
0.12
ND
*ND = not determined
Bottom Organisms
The number of organisms per square meter of the lake bottom area ranged
from 0 to 2,451. Aquatic earthworms, chironomids, and nematodes were
three predominant organisms in the lake sediments. Most of the orga-
nisms detected were aquatic earthworms of the family Naididae which
are characteristic of shallow and turbulent waters. Chironomid worms
were sparingly present in areas where organic solids were present in
the mud. They were conspicuously absent in locations where log rafts
42
-------
were formerly tied up. At these locations (in the Lake River), a
great deal of bark and wood chips were sieved from the bottom sedi-
ments but relatively few living organisms were found.
The significance of the biological invento'ry of the bottom organisms
lies in the fact that these organisms are more or less fixed in their
habitat and cannot move to more favorable surroundings when pollu-
tional conditions become critical. Therefore, these organisms should
be good indicators of the past and present environmental conditions.1^0-'
43
-------
SECTION VII
WATER QUALITY PREDICTION APPROACH
Dredging of Vancouver Lake to make it deeper and introducing Columbia
River water into the lake through a channel or culverts are being
considered as possible methods of both increasing lake use potential
and as a water quality iinprovement measure. To predict the effect of _
the above measures on the final water quality in the lake, the following
information and steps were considered essential in approaching this
problem:
Water Quality in the Columbia River - Vancouver Lake System
It was essential to establish the available water quality in the
Columbia River and the existing water quality in the lake in order_to
predict the obtainable water quality in the lake if the Columbia River
water were diverted into the lake. 'The available water quality in the
Columbia River has been established in Section V. The existing water
quality in Vancouver Lake was established in a previous study. U^J A
summary of the water qualities in the two systems is given in Table 7.
Hydrodynamic Characteristics of Columbia River - Vancouver Lake System
In addition to the information on water quality, the information on
the hydrodynamic characteristics of the system under the present condi-
tions as well as under the proposed modification of the Columbia River-
Vancouver Lake system was equally important.
The information on the hydrodynamic characteristics of the system was
obtained through concurrent but three separate studies. (-4'b'bJ These
studies were involved in acquiring hydrologic and hydrographic field
data which were then used in the construction, operation, and verifi-
cation of the hydraulic model.
A summary of the results is presented here, and the readers should
refer to the above mentioned three studies for detailed information.
During August, the water quality conditions were critical because of
low flows and high temperatures. Therefore, the conditions for the
month of August were emphasized:
• The tidal relationships in the Columbia River-Vancouver Lake-
Lake River system are very important factors in the evaluation
of the flow rates into and out of Vancouver Lake. Seasonal
changes in depth of Vancouver Lake associated with net tidal
flows in Lake River are shown in Figure 17.
45
-------
Table 7. COMPARISON OF AVERAGE WATER QUALITY OF
VANCOUVER LAKE AND COLUMBIA RIVER
(Units are mg/1 unless otherwise specified)
BOD5
COD
Kjeldahl - N
N03 - N
Total P as P04
TS
TVS
Conductivity (y-mhos)
pH
hardness as CaCO,
so4
Cl
Temperature (°C)
DO
Coliform Bacteria
(median value - No/ 100 ml)
1 Fecal Coliforms
Blue -Green Algae
Vancouver Lake
8.0
12.0
2.25
0.17
0.70
200
90
170
6.7-9.3
104
14.5
4.0
4-26
5.7-14.8
3000
10-40
95
Columbia River
1.0
5.8
0.16
0.19
0.23
116
34
167
7.6-8.2
63
6.6
4.1
4-21
8-12
>200
>30
0.5
(% of total algae)
State of Nutrition
eutrophic
mesotrophic
46
-------
12
10
L
*
-
U
:-
:
c
^_
§6
UJ
tr
u
h
<:
LEGEND
Water depth of
the lake
Net inflow to
the lake
Net inflow
from the lake
-rf-L
:
300
35CV
2003
150 2
I
ICO?
-
50
M A M J J A S
MONTH OF A YEAR
Figure 17. Mean Seasonal Variations in Lake Depths and Net Infloiv-
Outflow Rates of Lake River to Vancouver Lake for
Existing Conditions.
47
-------
Statistical analysis of field water stage data indicated that
in August the average high elevations of the Columbia River,
Vancouver Lake, and Lake River (at Felida) were 5.78, 4.41, and
4.91 feet above mean sea level.
The average value of the differences in peak water surface
elevations between the Columbia River and Vancouver Lake during
August was about 1.8 feet, while the average values of the tidal
fluctuations in the Columbia River and Vancouver Lake were 2.25
and 0.15 feet, respectively. This information was the basis
of the sinusoidal tide variations in the Columbia River and Lake
River as used in the water quality simulation study.
The difference in elevation between the Columbia River and
Vancouver Lake is influenced by the general rising and falling
trend in the Columbia River stage. This relationship shows
that Vancouver Lake rarely goes below a stage of about four feet
due to the tidal flat at the entrance to Lake River, and the
Columbia River maximum elevation is sometimes less than the
Vancouver Lake minimum elevation.
The main rivers and creeks which play an important role in influ-
encing the quantity and quality of Vancouver Lake are: (a) the
Columbia River, (b) the Willamette River, (c) the Lake River,
(d) Salmon Creek and Burnt Bridge Creek. The estimated flows
of these streams and the approximate contribution of groundwater
and precipitation are shown in Figure 18.
The hydraulic model study indicated that introduction of the
Columbia River water into the lake produced near complete
mixing conditions. The results of a typical test are shown in
Figure 19. In this test, a precalculated dose of a fluorescent
dye was completely mixed with the lake water and then the
Columbia River water was introduced into the lake. The dye
concentration in the model was measured as function of time at
seven stations in the lake and at the inlet to Lake River. A
total of 22 tests were conducted under various conditions of
stream flows, tidal variations and dredged depth.
It was established that in order to prevent the tidal flow
from Lake River into Vancouver Lake, the width of the proposed
channel connecting the Columbia River and Vancouver Lake should
be 150 feet or greater.
The relationship of average detention time in the lake of the
average inflow introduced into the lake under various lake
bottom dredged conditions is shown in Figure 20.
48
-------
I00*cfs
20*cfs
20* cfs
I94,500**cfs
29,400 cfs
A Salmon Creek--100* cfs. Flow moves upstream or downstream
depending on tidal action and stage trend in Columbia River.
B Lake River--300* cfs in and out. Tidal flow plus Salmon
Creek half of the time.
C 20* cfs ground water
D Vancouver Lake--12 cfs precipitation on lake
E Burnt Bridge Creek--20* cfs
F Columbia River--194,500** cfs
G Willamette River--29,400 cfs
H Proposed Site for Diversion of the Columbia River Water
into Vancouver Lake
*Estimated
**At Dalles, longer record
Figure 18, Average Annual Flows
49
-------
100
• ii
o
o
>v
o
80
QC
t
UJ
o
o
o
UJ
o
UJ
UJ
a:
60
40
20
'
n
o
Sampling stations scattered
throughout the lake
-
Columbia River inlet to the lake
Vancouver Lake outlet
20
40 60 80
MODEL TIME, MINUTES
100
120
Figure 19. Relative Concentration of Dye in
Vancouver Lake Model as Function of Time
140
-------
100
Conditions:
ake surface area - 105x10" sq ft
Lake bottom dredged to:
-20 ft msl
2000 4000 6000 8000 10000
AVERAGE INFLOW TO LAKE, cfs
12000
Figure 20. Lake Detention Time and Average Inflow
through Any Kind of Conduit(s)
-------
Water Quality Indicator
After acquiring the water quality and quantity information, the next
step was to select a water quality parameter which would be indicative
of the overall water quality in the lake and at the same time the
parameter selected could be described mathematically in terms of its
relationship with other factors affecting it. Dissolved oxygen was
the water quality parameter selected as an indicator of the overall
water quality in the lake because of the following reasons:
a.
dissolved oxygen is essential for aquatic life,
b. aquatic plant photosynthesis and atmospheric reaeration are the
sources of dissolved oxygen in an aquatic system, and the addition
of dissolved oxygen by these processes can be described mathematically,
c. the sinks of dissolved oxygen in an aquatic system are respiration
by microorganisms and other aquatic life and decomposition of
organic matter. These sinks can also be written into approximate
mathematical equations,
d. the fact that interaction of phosphorus, nitrogen, carbon dioxide,
other trace nutrients, sunlight, temperature, etc. with phyto-
plankton results in the production of photosynthetic oxygen; that
the atmospheric reaeration of aquatic systems depends upon the
wind action, temperature, water depth, and the dissolved oxygen
deficit; that the depletion of dissolved oxygen is related to
biochemical oxygen demand of aqueous and benthic zones including
respiration of bacteria, algae, zooplankton, fish, and other
organisms suggest that the dissolved oxygen is indeed a water
quality parameter which indicates a composite effect of many of
the dominant processes that take place in a dynamic aquatic
ecosystem,
e. the measurement of dissolved oxygen can be made easily and accurately,
and
f. dissolved oxygen is one of the most important water quality standards.
Therefore, the main emphasis in this study was placed on the dissolved
oxygen model although phytoplankton and bacteria models were also
attempted.
Water Quality Model
Computer programming and digital computers have made it possible to
build simulation models of dynamic ecosystems. The accuracy of these
models depends largely on the accuracy of the various coefficients used,
the assumptions made, and the functional relationships incorporated.
52
-------
The water quality model considered in this study consists of two main
parts: DO Model and Aquatic-Life Model. The emphasis in this study
has been placed on the DO Model because of the better understanding
as well as the wide acceptance of the mathematical relationships
involved. Although the two models are interrelated, the response in
terms of change in population of organisms as related to changes in
environmental and nutritional factors is difficult to predict under
the present state of knowledge, and it becomes even more difficult to
predict the number of biological species and the population of each
of the species. On the other hand, dissolved oxygen as related to
environmental and nutritional changes can be estimated.
BO Model: Several modifications and improvements to the earlier
DO model by Streeter-Phelps(27) have been suggested/-28>29»^>lii
The DO model considered in this study was primarily based on'the
work of Chen(34) and Chen and Orlob. (•") However, we found that
we could not verify the model with the actual field data unless
the temperature dependence of phytoplankton growth rate (y) was
included. The temperature effect was especially important for
predicting diurnal variations in dissolved oxygen.
The mechanisms considered which affect the DO concentration are
advection (oxygen in inlet streams minus outlet streams to
Vancouver Lake); photosynthesis as affected by nutrients, light
availability, and temperature; biological respiration and
deoxygenation; and atmospheric reaeration. A mass-balance type
formulation which incorporates major processes that affect dis-
solved oxygen is presented:
Rate of
Change of
00 Mass Rate Change in DO Mass Due To
T + (y - r)pVT/R - K V£ - KJ)A + K?(0 - 0)V
O _L T- i S
Advective Net Biochemical Benthic Reaeration
Transfer Photosynthesis Oxygen Oxygen
Demand in Demand
Water
[1]
where V = the volume of the lake;
t - time;
TQ = the total advective transfer of oxygen defined as the
summation of QgOg, QC0C, and QiC^, in which Ot>, Oc,
and Oi are the oxygen levels of Burnt Bridge Creek,
the channel or culverts, and Lake River, respectively;
T = the lake water temperature;
0 = the dissolved oxygen concentration in the lake;
R = the conversion factor between oxygen and algal biomass;
55
-------
I = the biochemical oxygen demand;
K! = the decay coefficient for BOD;
K£ = the reaeration coefficient;
K^ = the oxygen uptake by detritus;
y = the specific growth coefficient of phytoplankton
(algae) ;
r = the respiration coefficient of phytoplankton;
D = detritus concentration accumulated at the lake bottom;
p = the biomass concentration of phytoplankton; and
Os = the dissolved oxygen saturation concentration.
The correlated components which directly or indirectly affect the
dissolved oxygen are biomass of phytoplankton, organic and inorganic
nutrients, and zooplanktons . These components are described by a
series of mass balance equations as follows:
Biomass of phytoplankton. The biomass of phytoplankton is trans-
ported by the movement of water- -advection. In addition, phyto-
plankton growth rate is determined by light, temperature, and
nutrient conditions. It decreases as a result of continuous
respiration, settling, and grazing by zooplankton. Those terms
must be included in the mass balance equation to form a differ-
ential equation for phytoplankton which directly affect the DO
level in equation [1] .
Rate of
Change of
Phyto- Rate Change in Phytoplankton Mass
plankton Due To
Mass
= T + [(„ - r)T]PV(l - s) - gTzV/Y [2]
Ly L*
Advective Net Growth After Grazing of
Transfer Settling Phytoplankton
by Zooplankton
where T_ is the total advective transfer of biomass of phyto-
plankton, s the fraction of settling of phytoplankton, g the
specif i. growth coefficient of zooplankton, Yz the yield
coefficient of zooplankton, z the total count of zooplankton,
and \i is the specific growth coefficient of phytoplankton which
is assumed to follow the Michael is -Men ton kinetics for the
uptake of limiting nutrients or light. In this study, nitrogen,
phosphate, and light intensity are considered as possible
limiting factors
r_,
[3]
54
-------
in which y is the maximum possible growth rate; 1C , K,,, and Kp are
the Michaelis-Menton constants and are respectively the concentration
of light, nitrogen, and phosphate at which u equals 0.5 y.
According to Beer's law, the solar energy reaching the water surface
is attenuated exponentially with water depth influenced by the
suspended silt and phytoplankton population. A sinusoidal model
as the function of photoperiod was used in this study.
L = LQ exp [-(a + bp)y] , [4]
and
/TT(t - t_)\
[5a]
= 0 tsr>t>tss [5b]
where L is the light intensity in Langleys/day* at the depth y
measured downward from the water surface, LQ the solar energy at
water surface at time of day t, L the solar energy at noon time,
C^ the degree of cloud cover, tsr the time at sunrise, and tss
the time at sunset.
For the completely mixed model in the lake of H feet in depth,
the average value of light intensity, L, was calculated by
- exp [(-a - pb)H] rfi,
H(a + pb)' L J
Biomass of zooplankton. The growth and death rates due to natural
causes were presumed to be directly proportional to the water
temperature. Mass conservation for biomass of zooplankton may be
expressed as follows:
Rate of
Change of Rate Change in Zooplankton Number
Zooplankton Due To
Number
T + gzVT - mzVT - yFV/yf [7]
«L- J-
Advective Growth Mortality Predation
Transfer by Fish
_?
*0ne foot-candle = 3.2675 x 10 Langleys/day. Calibration of the
instrument used in the Vancouver Lake study is 4 micro-amp for 1
foot-candle. Therefore, 1 micro-amp = 8.1686 x 10~3 Langleys/day,
55
-------
in which TZ is the total advective transfer of zooplankton, m the
mortality of zooplankton, y the specific growth rate of fish, F
the biomass of concentration of fish, and Y£ the yield coefficient
of fish. Predation of zooplankton by fish was excluded in the
simulation study.
Biochemical oxygen demand. The mass balance equation for BOD
which directly affects the DO level may be written as
Rate of
Change of Rate Change in BOD Mass
BOD Mass Due To
= T^ - KjVl - K3V* [8]
Advective Removal of Removal of
Transfer BOD by Aerobic BOD by
Bacteria Settling
where T is the total advective transfer of BOD, K, the rate of
BOD removal by sedimentation and/or adsorption, and I the BOD
concentration.
Nutrient level. Nutrients can be consumed by phytoplankton (sinks),
but released by zooplankton and recycled by bacteria from lake
bottom deposits (sources)„ The conservation of mass for any given
nutrient becomes:
Rate of
Change of Rate Change in Nutrient
Nutrients Due To
Tn + azV + 3DA -
Advective Recycling Recycling Conversion
Transfer by Zoo- by Bottom of Nutrient to
plankton Sediments Phytoplankton
in which n is the concentration of nutrient at time t, T the
advective transfer of nutrient, a the return coefficient of
nutrient from zooplankton, g the recycle coefficient from bottom
deposits depending upon the rate of bacteria metabolism, and Y
the yield coefficient of phytoplankton for a specific nutrient"
Dissolved oxygen saturation concentration. The dissolved oxygen
saturation concentration is a function of temperature, barometric
pressure, and salinity of water. The changes in DO concentrations
in Vancouver Lake due to fluctuations in barometric pressure were
56
-------
assumed to be negligible. However, if one wishes to include
this effect, the following equation can be used:
°s = °s 76irH^
where p is the water saturated pressure in mm o Hg at a partic-
ular wa¥er temperature T in °C, Og is the saturated value of
dissolved oxygen at barometric pressure of p1 in mm of Hg, and
0 is the dissolved oxygen saturation concentration at a baro-
metric pressure of 760 mm of Hg.
An empirical formula for QS as a function of temperature as given
below for fresh water was used in this study.
0 = 14.652 - x.1002 x lO"1! + 7.9971 x lO'^2 [11]
- 7.7774 x 1(T5T3
Aquatic Life Model: Parker!s(36) work on modeling of Kootenay Lake
in British Columbia was the basis of the aquatic life model attempted
in this study. Some modifications of Parker's model to correspond
to conditions in Vancouver Lake were made.
The available quality data indicate that Vancouver Lake is currently
undergoing rapid eutrophication. Therefore, the seasonal vari-
ations in quantity of algae as well as bacteriological level are
of importance and are described as follows:
Algae. The seasonal variations of algae and its affected
factors such as zooplankton and phosphate density are repre-
sented as:
Change Rate Change in Algal Mass
of Algal Due To
Mass
P P - p?T - p,zT > [12]
L
P
Growth Natural Grazing of
Death Algae by
Zooplankton
57
-------
Rate of Change
of Zoo-
plankton
Number
dz
cEw
= z
Rate of
Change of
Phosphate
Concentration
Rate Change in Zooplankton
Number Due To
/T-13^'
P PG(P
P P
Growth
Rate Change in Phosphate
Concentration Due To
z2TG(Pp)
Natural
Death
[13]
V
Advective
Transfer
r2 dw
Conversion
to Zoo-
plankton
"3 dw
Conversion
to Phyto-
plankton
[14]
where w is the week of the year; (X the net flux to the lake;
Pl» P?» PV zi» Z2> p?> and P^ are constants; PB the phosphate
of the incoming flow; Pp the photoperiod (or daylight hour);
GCP,,) the function of photoperiod; and T the water temperature
of the lake. Some of these are represented as:
G(Pp)
= 12.2 + 4.1 sin 2v
= 0.82 + 0.343 sin
'38_-w\
V~^"/J
/P - 7.2'
T P10.4
[15]
[16]
From the available field data, the incoming flow rate of Burnt
Bridge Creek, Qg; phosphate content of Burnt Bridge Creek, Pg;
and the lake water temperature were found to be represented
as the following functional relationships.
= 28.32
-------
Equations [18] and [19] are for w (time in weeks) greater than
or equal to 8; otherwise w is replaced by (w + 52) in the
equations.
Total bacteria. It is assumed that the bacteria depend on BOD
as the food source. The mass balance for bacteria and sub-
strate is given as:
Rate of
Change of
Bacteria
Mass
dB
3w
Rate Change in Bacteria
Mass Due To
(y - k?T)B
LJ
Net Growth
QB
BB
v
Advective
Transfer
[20]
Rate of
Change of
Substrate
dS
QS
BB
v
Advective
Transfer
Conversion
to Bacteria
H pqksTB [21]
Release of Sub-
strate Due to
Bacteria Death
and Lysis
where B and S are the total bacteria count and substrate concen-
tration, respectively, k? the rate of die-off of bacteria, SB
the substrate concentration of the incoming flow, p the fraction
of cells which die in the lake, q the fraction of exogenous sub-
strate released per unit cell lysed, and Ys the effective yield
coefficient of substrate. The specific growth rate of bacteria
y is expressed as:
y exp -0.5
: - 261
5.5
[22]
in which y is the maximum specific growth rate of bacteria. An
approximate maximum value of pq has been reported by Postgate^'J
to be 0.004. Sayer(38) and Gellman and Heakelekianv-^J have
shown that 0.5 gram volatile suspended solids is synthesized per
gram of BOD5 removed. Therefore, the value of 0.5 for Ys is used.
59
-------
Method of Solution
Following the formulation of water quality model for the simulation
study, the numerical solution to a set of differential equations was
obtained in a step-by-step manner with the aid of a digital computer.
The finite difference method was applied to the solution of DO model
and a third order Runge-Kutta method was used for the aquatic life
model. Initial conditions were required for solving the mathematical
models and to simulate the various subsequent behaviors in the system.
Initial lake water quality, climatological data, flow quality and
quantity, rate constants of biological activities, physical dimensions
of the lake, etc., were necessary.
When the initial input data were ready, the explicit technique of
numerical integration was used by substituting all the conditions
corresponding to the initial time in the right-hand side of
equations [1], [2], [7], [8], and [9], and for the time derivatives
on the left-hand side. Once the time derivative of a given variable
was known, it was evaluated for some short time interval by assuming
a constant rate of change in this interval. The new values became
the initial conditions for calculating the next set of conditions
over the next time interval. The solution was thus obtained in time
increments At until the desired total simulated time had been reached.
The detailed steps of the method are given in Appendix D.
Table 8 summarizes the values of various reaction rate constants and
other coefficients used in the solution of the water quality model.
A number of assumptions were made in the solution of mathematical
models:
• Complete mixing conditions were assumed in Vancouver Lake.
Previous studies(3) indicate that the lake is unstratified
most of the year because of its shallowness and mixing
induced by wind action. It is believed that even if the lake
is dredged to a water depth of 15 feet, complete mixing
assumption will still prevail.
• The euphotic zone exists to a depth of three feet. Field
data indicated that the penetration of sunlight was limited
to water depths less than three feet.
• The biochemical and biological reactions follow first order
equations.
• The transport mechanism of diffusion is small compared to
advection and other transport mechanisms for non-conservative
soluble substances.
• Daily sinusoidal cyclic variation of tides in the Columbia
River and Lake River was assumed. Magnitudes of the mean
tidal amplitude were obtained by statistical analysis of the
field hydrographic data.
60
-------
Table 8. FUNCTIONAL OR ESTIMATED COEFFICIENTS FOR WATER QUALITY MODEL
Parameter
Functional Relationship
or Estimated Coefficients
A. DO MODEL
Light Extinction
a: Background, per foot
b: Algal suspension, per foot per mg/1
Ci : Degree of cloud cover
L: Average light intensity, Langleys/day
L : Solar energy at noon time, Langleys/
day
P : Photoperiod, day
t : Time of sunrise, day
Evaporation
C^: Empirical constant
C,: Empirical constant
Nutrient
a: Return coefficient of nutrient from
zooplankton
0.09
0.006
0.40
/I - exp[(-a-bpjH]\
olH(a+bp)/
400
0.5
0.2917
0.394
-0.098
0.01
Reference
and Remark
Chen
(34)
,(34)
Chen'
Assumed in this study
Calculated from Beer's
Law
Computed from data by
Bhagat and Funk^J
Assumed in this study
Assumed in this study
Jaske
Jaske
(40)
(40)
Assumed in this study
-------
Table 8. Continued
Parameter
Functional Relationship
or Estimated Coefficients
Reference
and Remark
o\
tsj
B: Recycle coefficient from bottom depos-
its depending on the rate of bacteria
metabolism
YpN: Yield coefficient of phytoplankton
for nitrogen
Y p: Yield coefficient of phytoplankton
^ for phosphate
BOD decay coefficient, per day
K2, reaeration coefficient, per -day
K3, rate of BOD removal by sedimentation and/or
absorption, per day
0.01
12.0
24
(Ki)T =
6, = 1.047
(Kl)
20
K! -
(K2)T =
62 =
K2 =
K2 -
0.1
0.231
0.25
0.20
1.046
0.25
0.40
T-20
T-20
Assumed in this study
McGauhey et al.
(41)
Deduced from Parker
(36)
Temperature dependent
Streeter and
Pence et al
(-43-)
Orlob et al.
Temperature dependent
O'Connor and Dobbins'-44^
Orlob et al. (-43-)
Assumed in this study
-------
Table 8. Continued
p
Functional Relationship
or Estimated Coefficients
Reference
and Remark
Phytoplankton
r: Respiration coefficient, /day/degree
s: Settling fraction
R: Oxygen and algae conversion factor,
mg algae per mg 02
\t: Maximum possible growth coefficient,
per day per degree
1C : Coefficient in Langleys/day
K,,: Coefficient in mg/1
K : Coefficient in mg/1
Zooplankton
m: Mortality, per day per degree
Y : Yield coefficient of zooplankton,
no. of zooplankton per mg algae
g: Specific growth coefficient of
zooplankton, per day per degree
KI+: Decay of bottom deposits, per day
0.025
0.07
0.633
0.090
43.2
0.0088
0.005
0.025
12.0
0.02
0.007
Assumed in this study
Bella C«>
Estimated from data by
Bhagat and Funk(3)
Chen
'34)
McGauhey
McGauhey
^ ^
^ '
Assumed
Assumed
-------
Table 8. Continued
Parameter
Functional Relationship
or Estimated Coefficients
Reference
and Remark
o : Saturated dissolved oxygen, mg/1
14.652 - 0.41002 T
0.0079971 T2 -
0.000077774 T3
o\
B. AQUATIC LIFE MDDEL
P : Photoperiod, hr
G(P ): Function of photoperiod
QR: Flow rate in Burnt Bridge Creek,
liter/sec
12.2+4.1sin
fP -7.2Y1
0.82+0.343sin 2-rt
28
i_
.32^16.2-15.7
?• Phosphate content in Burnt Bridge 150+750 exp
B
Creek, micro-gm/1
T: Water temperature in the lake, °C 4.0+22 exp
f-O 5^
L v .
y: Maximum specific growth rate of
bacteria, per day
pq: Substrate release by bacteria
k '. The coefficient of die-off
bacteria, per day per degree
0.055
0.004
0.0088
Parker
(36)
Parker
(36)
Calculated for this
study
Calculated from data by
Bhagat and Funkv3)
Calculated from data by
Bhagat and FunkC3)
Assumed in this study
Postgate^37''
Assumed in this study
-------
Table 8. Continued
en
Functional Relationship Reference
Parameter or Estimated Coefficients and Remark
V-
b
P :
V
P :
3
lr
Z2:
V
P.:
The effective yield coefficient of the
substrate, mg bacteria per mg substrate
released
Growth rate coefficient of algae
Natural death coefficient of algae
Predation death coefficient of algae
by zooplankton
Growth rate coefficient of zooplankton
Natural death coefficient of zooplankton
Phosphate utility rate by zooplankton
Phosphate utility rate by algae
0.5
0.00012
0.002
0.006
0.0015
0.03
0.6
20.00
Gellman et al. ^9)
Parker ^ '
Parker (36)
Parker'-36-'
Parker ^
Parker ^ ^
n 1 (36)
Parker J
Parker *
-------
• A constant lake surface area was assumed. This was verified
by comparing tidal inflow with volume change in the lake.
• The change in the dissolved oxygen saturation concentration
due to the local barometric pressure fluctuations is negli-
gible.
• Average evaporation rates for each incremental period were
used in the analyses.
• The effect of fish biomass on the zooplankton population was
neglected.
• Atmospheric aeration and photosynthesis mechanisms were
limited to the upper three feet of the lake water even after
dredging of bottom sediments.
• Deoxygenation coefficient (K-,) and reaeration coefficient
vary with temperature according to the accepted relationship
T-20
K20°
• Numerical values of various constants and reaction rates as
given in Table 8 were used in this study.
Verification of Water Quality Model
After formulation of mathematical equations and the establishment of
the method of solution of these equations, the next step was to
generate the theoretical data with the aid of a digital computer and
to check the validity of the mathematical model. The validity of
the model was evaluated by comparing the theoretical values with the
observed field data. It is obvious that the mathematical model is
not of much value unless it is verified with the actual field obser-
vations. If the difference between the computed and the observed
values is significant, then the modification of the mathematical
model should be continued until this difference is reduced to a
minimum value. This procedure was followed in this study and, hence,
involved trials of several numerical values of a coefficient until
the difference between the computed and observed data reached a
minimum. It should be pointed out that the values of some of the
coefficients were available for the Vancouver Lake System, whereas
the values of other coefficients suited to this system were derived
from the literature. Trial procedure was essential in order to
arrive at a value characteristic of the Vancouver Lake System in the
case of a coefficient the magnitude of which was reported in the
literature to vary over a wide range. These trials were also helpful
in revealing the relative sensitivity of the coefficients tried.
66
-------
For the purpose of verification of the DO model, dissolved oxygen
concentration and temperature readings were recorded on a continuous
basis for the month of August, 1970. This month was selected
because the water quality in Vancouver Lake generally reaches a
low point during this time because of low \\rater level and high
temperatures. A typical comparison between computed and observed
DO levels is shown in Figure 21. On the i^hole, the computed values
were very close to the observed values. The peak DO values observed
in the afternoons of summer months which are typical of eutrophic
lakes and other bodies of water were at times significantly different
from the corresponding simulated values. Generally, we are concerned
with the lowest dissolved oxygen concentration reached in a system
and the difference between the lowest simulated and observed values
was less than 1.0 mg/1.
The aquatic life model was verified against the limited observed
data collected in 1967.(3) The results are shown in Figures 22 and
23. The hallow circles represent data at different locations in
Vancouver Lake observed on the same date, whereas the solid black
circles represent average values for the entire lake. Because of the
limited field data available, there is a further need of verification
of the aquatic life model.
Upon verification of the water quality model under the existing
prototype conditions, the model is ready for application to the
predictions of water quality that can be expected under variety of
modifications to the Vancouver Lake-Lake River-Columbia River System.
67
-------
>
-
10
o>
8
UJ
o
0
UJ
o
en
FIELD DATA
/ IN 1970
SIMULATED
DATA
12 4 8 12 4
AM AUG. 13,1970
8 12 4 8 12 4
AM AUG. 14, 1970
8
Figure 21. Comparison between Simulated and Observed Dissolved Oxygen
Concentration in Vancouver Lake.
-------
E7
x.
Q. O
ro
O
D
O
_J
<
Initial Conditions:
pt = 0.0267 mg/1
zi - 4.0 no/1
P. = 200 micro-gram/1
— Simulated data
§ Average field data
D Field data from
Bhagat and FunkC3)
0 10
JANUARY
20 30
TIME, weeks
40 50
DECEMBER
Figure 22. Comparison between Simulated and Observed Alpal Concentration in
Vancouver Lake.
-------
O
_ 40
6
O)
QL
10
O
UJ
I-
O
<
CD
30
z
§ 20
<
10
0
Initial Conditions:
Bi = 0.013 mg/1
Si = 3.00 mg/1
— Simulated data
• Average field data
3 Field data from
Bhagat and FunkC3)
0 10
JANUARY
20 30
40 50
DECEMBER
TIME, weeks
Figure 23. Comparison between Simulated and Observed Total Bacteria
Concentration in Vancouver Lake.
-------
SECTION VIII
PREDICTION RESULTS AND DISCUSSION
Under the present conditions, the dissolved oxygen level in Vancouver
Lake frequently goes down to about 6 mg/1 during the night and sometimes
the level is as low as 4 mg/1. If the lake is dredged to 10 feet below
mean sea level to provide 15 feet of water depth and there is no curtail-
ment in the existing levels of inflow pollution loads to the lake, then
the water quality in the lake will become worse and the DO model pre-
dicts that the dissolved oxygen level in the lake will frequently go
down to 4 mg/1. On the other hand, if Columbia River water is also
introduced, then the water quality in the lake is predicted to improve
according to Figure 24. Here the dissolved oxygen concentration in the
lake is plotted as a function of the detention time in the lake of the
introduced Columbia River water. The detention time is inversely pro-
portional to the flow rate of the introduced water (Figure 20). In
order to raise the present level of dissolved oxygen in the lake to
8 mg/1 (as required for class A lakes), an average flow of 750 cubic
feet per second will be required to be diverted from the Columbia River
to Vancouver Lake near its southwest corner. This prediction is based
on the assumption that the water quality of the Columbia River will
remain of as high quality as is today. The Columbia River is an inter-
state stream and is regulated by state agencies from Washington and
Oregon through federally approved water quality standards and plans of
implementation. It is therefore believed that the water quality of the
Columbia River will be maintained and possibly improved.
A summary of the water quality input data used in the water quality-
model for model verification and for prediction analysis is given in
Table 9. These data were used as the initial values in the generation
of theoretical values of time-varying water quality parameters for the
subsequent time periods. The average concentrations of nitrogen and
phosphorus, in the Columbia River, that are considered easily available
to plankton were used. The easily available forms of nitrogen consid-
ered were NH3, N02, and NOs, and the similar form of phosphorus
considered was the orthophosphate. In the case of present nutrient
levels in Vancouver Lake', high total phosphorus values and average
total nitrogen values were used in order to compensate for the recycling
of nutrients from bottom sediments. High phosphorus values rather than
average values were chosen to simulate the critical conditions in the
lake, and phosphorus is considered to be the most important of the
limiting nutrients for the blue green algae (Aphanizomenon Flos-Aquae)
which are prevalent in Vancouver Lake.
Attempts were also made to predict the concentrations of algae and
bacteria in Vancouver Lake for the post-modification of the system.
The results are shown in Figures 25 and 26. These results are based
on the organism concentrations in the Columbia River water as shown in
these figures and, for other concentrations than these, proper modifi-
cation of the predicted results will be required.
71
-------
8
o»
E
LJ
Dredging of Vancouver Lake bottom
to 10 ft below msl and assuming
current levels of water quality
for summer conditions, with flushing
water from the Columbia River
(SJ
X
o
o
UJ
>
o
Existing Conditions, Det. time > 6 months
,1
10
Dredged lake without any flushing water, Det. time = 3 years
50
20 30 40
DETENTION TIME, DAY
Figure 24. ' Predicted Water Quality in Vancouver Lake
60
-------
Table 9. WATER QUALITY INPUT DATA USED IN WATER
QUALITY NDDEL FOR VERIFICATION AND PREDICTION
Water Quality
Total phytoplankton (mg/1)
Nitrogen (mg/1)
Phosphate (mg/1)
Dissolved oxygen (mg/1)
Total zooplankton (no/1)
BOD5 (mg/1)
Burnt Bridge
Creek
8.0
4.22
6.34
8.6
20.0
10.0
Vancouver
Lake
8.0
2.3
1.6
5.7
20.0
8.0
Columbia
Rivera
4.0
0.24
0.12
9.0
2.0
2.0
r\
Used for prediction after the Columbia River water is diverted into
the lake.
There are three interrelated steps which can be taken to improve the
quality and quantity of water in Vancouver Lake:
(1) curtail the sources and amounts of pollution entering the lake,
(2) dredge the lake to remove the nutrient rich bottom sediments
and to increase the depth, and
(3) introduce an additional flow of better quality water into the
lake to improve and then to maintain its quality.
The study of the last two steps and their effect on the water quality in
Vancouver Lake was the main emphasis of this study and, although step
number one was not in the scope of this study, a few comments may be in
order. The sources of pollution to Vancouver Lake include Burnt Bridge
Creek, Lake River, and drainage from livestock and agricultural areas.
Burnt Bridge Creek has been receiving drainage from septic tanks which
serve approximately 20,000 people. Today about 45% of the area popu-
lation is served with municipal sewers and within the next five years
the remaining population of the area is expected to be sewered. There-
fore, the completed and the planned sewer installation programs and
completed and planned facilities for treatment of wastewaters should
reduce the level of pollution in Burnt Bridge Creek and hence should
reduce the amount of human waste entering Vancouver Lake. To control
the drainage from livestock areas, better management of livestock
wastes is needed. By introducing the Columbia River water into the lake,
the tidal inflow to the lake from the Lake River will be reduced. At
present, Lake River transports into the lake, during high tidal cycles,
sediment and nutrient loads which it receives primarily from Salmon
Creek.
One of the potential uses of a simulation model is to perform sensitivity
analyses of variables operating on a system. Once the accuracy of the
model has been verified, the relative significance of the different
-------
300 r
O)
o.
-200
ID
O
O
100
<
h-
O
Conditions:
Wj = 50 ft
Ah = 1.5 ft
Bottom of lake dredged = -10 ft msl
Columbia River algal concentration =10 no/ml
Start flushing in January under existing
water quality conditions
0 10
JANUARY
20 30
40 50
DECEMBER
60
TIME, weeks
Figure 25. Predicted Effects of Dredging and Flushing on Total
Algal Count in Vancouver Lake.
-------
6 r
•
i
D
O
°o
DC
O —
CD
-------
parameters may be assessed. In the DO model, it was found that the
diurnal variation of dissolved oxygen was very sensitive to the phyto-
plankton specific growth rate (p) parameter. An example of this is
shown in Figure 27. The numerical values of y were varied from 0.05
to 0.15 per day per degree centigrade and the y value of 0.09/day-°C
best simulated the conditions in Vancouver Lake and hence this value
was used in the prediction analysis of Vancouver Lake.
This study though directed to the specific case of Vancouver Lake, the
systems analysis techniques developed, the models used, and the
approaches taken should be useful in the investigations dealing with
the improvement of water quality of polluted lakes. It is believed
that the results of this study will be valuable in the initial as well
as in the final development stages of Vancouver Lake System,
76
-------
32
28
24
20
o»
E
o 16
12
8
O p. = 0.15 /DAY /°C
x /i = 0.09/DAY/°C
• t = 0.05/DAY/°C
0
O
XX
xx
I2M 4 8 I2N 4 8 I2M 4 8 I2N 4 8 I2M
TIME
Figure 27. Sensitivity of Dissolved Oxygen to
Phytoplankton Specific Growth Rate, u
77
-------
SECTION IX
ACKNOWLEDGMENTS
This study was sponsored by the Office of Research and Monitoring,
Environmental Protection Agency. Grateful appreciation is extended
to the people of the agency, particularly to Dr. Curtis C. Harlin, Jr.,
Chief of the National Water Quality Control Research Program.
Appreciation is also extended to the staff and graduate students of
Sanitary Engineering, Washington State University, who participated
in the field surveys, sample collection, and analysis, especially
Pat Syms, Paul Bennett, and Richard Condit. Appreciation is also
extended to the people of Clark College, and Vancouver Sewage Treatment
Plant for use of their laboratory facilities.
The assistance of Ken Engebretsen, Don Tilson, Man Kadow, and Birdie
Danley, who are associated with the Port of Vancouver, in providing
boat storage facilities, a floating platform for housing continuously
monitoring equipment, and other assistance, is sincerely appreciated.
Acknowledgment is extended to Dr. Cheng-Nan Lin for the valuable assis-
tance in the mathematical modeling and computer programming, and to
Dr. John Orsborn for providing the information on the hydrodynamic
characteristics of the system studied.
Sue Taylor's assistance in typing this report is sincerely acknowledged.
79
-------
SECTION X
REFERENCES
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and^Quality Studies of Vancouver Lake, Washington, College of
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WA 99163, September 1971.
2. Stevens, Thompson and Runyan, Inc., Engineers/Planners, Portland,
Vancouver Lake Complex Development Plan, September 1967.
3. Bhagat, S. K. , and Funk, W. H., Hydroclimatic Studies of Vancouver
Lake, Bulletin 301, College of Engrg. Res. Div., Washington State
University, Pullman, WA 99163, May 1968.
4. Orsborn, J. F., Hydrologic Study of Vancouver Lake, College of Engrg.
Res. Div., Washington State University, Pullman, WA 99163, September
1971.
5. Orsborn, J. F., Hydrographic Study of Vancouver Lake, College of
Engrg. Res. Div., Washington State University, Pullman, WA 99163,
September 1971.
6. Orsborn, J. F., Hydrauli_c_Ntodel___Studv of Vancouver Lake, A report
to the Environmental Protection Agency, Contract #16080 ERP, June 1972.
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8. Lincoln, John H. , and Foster, Richard F., Report on Investigation
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9. Mackenthun, K. M. , and Ingram, W. M., Biological Associated Problems
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11. Geldreich, E. E., et al., "Type Distribution of Coliform Bacteria in
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12. Kenner, B. A., et al. , "Fecal Streptococci--Cultivation and Enumer-
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15, 1961.
81
-------
13. Reasoner, D. J., Aquatic Bacteriology of the Snake River, M.S.
Thesis, Washington State University, 1969.
14. Graham, V. E. , and Young, R. I., "A Bacteriological Study of
Flathead Lake," Montana Ecology, 15:101-109, 1934.
15. Potter, L. F., "Planktonic and Benthic Bacteria of Lakes and Ponds."
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16. Potter, L. F., and Baker, G. E. , "The Microbiology of Flathead Lake
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17. Boyd, W. L., and Boyd, J. L., "A Bacteriological Study of an Artie
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18. Johnstone, D. L., "Bacteriological Populations in Oligotrophic and
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1969.
19. Johnstone, D. L., Unpublished data, 1972.
20. Morrison, S. M., and Fair, J. F., "Influence of Environment on Stream
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21. Jaunasch, H. W., "Vergleichende bakteriologische Unlersuchung der
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23. Ballinger, D. G., and McKee, G. D., "Chemical Characterization of
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24. Laterell, J. J., Holt, R. F., and Timmons, D. R., "Phosphate
Availability in Lake Sediment," J. Soil and Water Conservation,
p. 21-24, January-February 1971.
25. Buddhain, W., Cobalt as an Essential Element for Blue Green Algae,
Doctor's Thesis, Univ. of California, Berkeley, California, 1960.
26. Anderson, J. B., Evaluation of Stream by Biological Studies.
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1961.
82
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27. Streeter, H. W., and Phelps, E. B., "A Study of the Pollution and
Material Purification of the Ohio River," U.S. Public Health
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28. Dobbins, W. E. , "BOD and Oxygen Relationship in Streams," Jour.
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Quality - A Mathematical Model of Dissolved Oxygen Concentrations
in Fresh Water Streams," Univ. of California, Berkeley, August 1965.
30. Bain, R. C., "Predicting Diurnal Variations in DO caused by Algae
in Estuarine Water," National Symposium on Estuarine Pollution,
Stanford University, p. 250-279, August 1967.
31. Goodman, A. S., et al., "Use of Mathematical Models in Water Quality
Control Studies," Water Pollution Control Research Series, ORD - 16,
1966.
32. Rainey, R. H., "Natural Displacement of Pollution from the Great
Lakes," Science, Vol. 155, p. 1242-1243, March 1967.
33. Bella, D. A., "Dissolved Oxygen Variations in Stratified Lakes,"
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October 1970.
34. Chen, C. W., "Concepts and Utilities of Ecologic Model," Jour.
San. Engr. Div., ASCE, Vol. 96, No. 5A5, p. 1085-1097, October 1970.
35. Chen, C. W., and Orlob, G., "A Proposed Ecologic Model for an
Entrophying Environment," Report to the FWPCA by Water Resources
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36. Parka, R. A,, "Simulation of an Aquatic Ecosystem," Biometrics,
Vol. 24, p. 803-821, December 1968.
37. Postgate, T. R., and Hunter, T. R., "The Survival of Stored
Bacteria," Jour. Gen. Microbiol., Vol. 29, p. 233-263, 1962.
38. Sayer, C. N., "Biol. Treat. Sewage Ind. Wastes," Reinhold
Publishing Corp., New York, p. 3-17, 1956.
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p. 1196, 1953.
40. Jaske, R. T., "Digital Simulation System for Prediction of Water
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41. McGauhey, P. H., Rohlich, G. A., and Pearson, E. A., "Eutrophication
of Surface Waters - Lake Tahoe Bioassay of Nutrient Sources," First
Progress Report to FWPCA, May 1968.
42. Pence, G. D., Jeglis, J. M., and Thomann, R. V., "The Development
and Application of a Time-varying Dissolved Oxygen Model,"
National Symposium on Estuarine Pollution, Stanford Press, p. 537-
585, August 1967.
43. Orlob, G. T., Shubinski, R. P., and Feigner, K. D., "Mathematical
Modeling of Water Quality in Estuarial Systems," National Symposium
on Estuarine Pollution, Stanford Univ. Press, p. 646, 675, August
1967.
44. O'Connor, D. J., and Dobbins, W. E., "Mechanisms of Reaeration in
Natural Streams," Transactions, ASCE, Vol. 123, p. 641-684, 1958.
45. Bella, D. A., "Simulating the Effect of Sinking and Vertical
Mixing on Algal Population Dynamics," Jour. WPCF, Vol. 42, Part 2,
p. 140-152, May 1972.
46. Camp, T. R., Water and Its Impurities, Reinhold Press, N.Y., 1963.
47. Fair, G. M., Geyer, J. C., and Okun, D. A., Water and Wastewater
Engineering, John Wiley and Sons, Inc., New York, Vol. 2., 1968.
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84
-------
APPENDICES
Page
APPENDIX A - ALGAE FOUND IN COLUMBIA RIVER AT
STATION #1
APPENDIX B - ALGAE FOUND IN COLUMBIA RRTI-R AT
STATION #2
APPENDIX C - WATER QUALITY OF THE COLUMBIA RIVER
APPENDIX D - METHOD OF SOLUTION OF MODELS
\PPENDIX E - DISSOLVED OXYGEN KDDEL, AQUATIC LIFE
NDDEL
-------
APPENDIX A
ALGAE FOUND IN COLUMBIA RIVER AT STATION #1
Phytoplankton
Average Cell Concentration, No./ml
December February April June August
Diatoms
Achanathes sp.
Asterionella formosa
Asterionella sp.
Caloneis sp.
Cocconeis sp.
Cocconeis placentula
Cyclotella sp.
Cymbella sp.
Diatoma sp.
Diatoma hiemale
Fragilaria crotonensis
Fragilaria sp.
Frustulia sp.
Gomphoneis sp.
Gomphonema sp.
Gomphonema lanceolata
Gyrosigma sp.
Hannea arcus
Melosira varians
Melosira sp.
Meridon sp.
Navicula sp.
Navicula minus
Neidium sp.
Nitzchia sp.
Opephoea martyi
Pinnularia acuminata
Rhizosolenia sp.
Rhoicosphenia curvata
Stauroneis sp.
Stephanodiscus sp.
Surirella sp.
Synedra amphicephala
Synedra incisa
Synedra filiformis
Synedra sp.
Synedra ulna
Tabellaria flocculosa
89
15
483
38
1
3
28
175
1
2
32
<1
100
7
25
14
19
1
421
30
45
6
5
1
860
80
3
18
1426
31
1
3
249
1
4
1
68
30
186
61
54
1
104
86
190
40
477
87
-------
APPENDIX A
ALGAE FOUND IN COLUMBIA RIVER AT STATION #1
(cont.)
Phytoplankton
_ Average Cell Concentration, No. /ml
December February April June August
Tabellaria asteroides
Tabellaria sp.
Tetracyclus elliptica
Unident. diatoms
71
<1
134
80
--
—
64
55
—
36
Yellow Greens
Tribonema
36
10
692 146
Greens
Actinastrum sp.
Anki strode sinus falcatus
Chlorella sp.
Chlorococcum sp.
Closteridium sp.
Closteriopsis longissima
Closterium sp.
Coelastrum sp.
Docidium sp.
Echinosphaerella
Eudorina sp.
Genicularia sp.
Gloeocystis sp.
Gonatozygon sp.
Micractinium sp.
Netrium sp.
Pandorina mo rum
Pedistrum duplex
Pediastrum sp.
Phacus sp.
Pleurotaenium sp.
Protococcus sp.
Rhizochonium
Scenedesmus quadricauda
Scenedesmus sp.
Sphaerocystis schroeteri
Staurastrum sp.
11
7
6
-~
1
--
10
2
64
31
<1
4
<1
2
3
51
-------
APPENDIX A
ALGAE FOUND IN COLUMBIA RIVER AT STATION #1
(cont.)
Phytoplankton Average Cell Concentration, No./ml
December February April June August
Ulothrix sp. --- -- -- 11
Volvox sp. -- -- -- --
Blue-Greens
Anacystis
Microspora -- -- -- 2°
Nostoc -- -- -- 10
Oscillatoria sp. — -- -- --
Oscillatoria angustissima
89
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APPENDIX B
ALGAE FOUND IN COLUMBIA RIVER AT STATION #2
Phytoplankton Average Cell Concentration, No./ml
December February April June August
Diatoms
Achanathes sp. 1 2 -- 4 --
Asterionella formosa -- -- -- 490 57
Asterionella sp. 99 5 534 24
Caloneis sp. -- -- -- -- 1
Cocconeis sp. -- -- -- 2 --
Cocconeis placentula -- -- -- -- <1
Cyclotella sp. -- -- -- 24 58
Cymbella sp. 4 -- 1 9 2
Diatoma sp. 10 -- -- 31
Diatoma hiemale
Fragilaria crotonensis <21 -- 215 787 249
Fragilaria sp. -- 25 108 76
Frustulia sp. -- -- -- |