INTERNAL REPORT 93
AQUATIC PRODUCTION IN A SOCKEYE SALMON-PRODUCING RIVER
Q. J. Stober and J. G. Malick
University of Washington
INTRODUCTION
The benthic invertebrate production and the fate
of allcchthonous
in the Cedar River have been under study since 1971.
Estimates of the benthos production will be incorporated in a model
of the lotic ecosystem and compared with estimates of production
material
obtained from unit watershed streams and larger rivers under investigation in the Coniferous Forest Biome. The study has been
coordinated from the start with concurrent Investigations in the
river drainage by the Washington State Department of Fisheries, the
Fisheries Research Institute (sponsored by the Seattle.City Water
Department), and the Municipality of Metropolitan Seattle (RIBCO).
In this report is summarized work completed in the first two years
of the study.
The upper Cedar River is maintained as a source of municipal water
supply by the City of Seattle. Water level is regulated to some
extent by means of the Masonry Pool Dam and the water supply diversion.
Masonry Pool Dam has a fixed spillway that does not allow regulation
of the lake level. However, there is an associated power house at
Cedar Falls where water is piped from the reservoir and released
into the river below. Two Pelton Water Wheel generators each pass
up to 350 cfs of water, the volume depending on the water level of
the reservoir. Flow is regulated at the water supply diversion by
removal of up to 372 cfs of water for municipal use.
Study Area
The Cedar River is a rather unique natural stream system by virtue of
its multiple
uses.
It was divided at the outset into three discrete
sections, and six invertebrate sampling stations were established along
these reaches (Figure 1). Five stations were in riffle areas closely
adjacent to established USGS gaging
stations.
Two stations were
located to yield data on production above Lake Chester Morse (the first
discrete section of river), one on the Cedar River (station 1) and the
other on the Rex River (station 2), the major tributaries to the Lake.
Below the reservoir the Cedar River is divided into two discrete sections
by the City of Seattle water supply diversion at Landsburg, and sockeye
salmon (Oncorhyncehus nerka) are excluded from the upper section; therefore,
two s ations were located along each of these two sections of river.
In the section above the diversion, stations were established near Cedar
Falls (station 3) and at Landsburq (station 4); and in the section below
the diversion, stations were established near Cedar Grove (station 5)
and near Renton (station 6).
1
MATERIALS AND METHODS
Benthic Invertebrates
Sampling was conducted in three ways for various periods
time. A
general survey of the invertebrate populations at each ofofthe
six
was made during the first three months of the study. Samples werestations
collected
each month beginning in June 1971 by means of a 0.25-m2 quadrat sampler
similar to that used by Surber (1937), from which the dominant taxa at
each station were established. In an effort to standardize stream invertebrate sampling methods with those used at Oregon State University by
Norman Anderson, sampling was also conducted by the method described by
Colemen and Hynes (1970). Screen pots were buried in the substrate with
only the surface exposed (Figure 2) at each station on July 13, 1971 and
were sampled monthly from September 1971 through October 1972. Pot
sampling below Landsburg was discontinued after 6 months because of
vandalism, and quadrat sampling was conducted instead for benthos at
stations 5 and 6. Drift samples were collected once a month at each
station for
a.24-hour period.
The samplers were of the design described
by Miller (1961) and were constructed of 16.6-cm-diameter fiberglass pipe
constricted at the mouth to 11.5 cm and fitted with a 1.6-m length of
351-P mesh netting. They were held in position in the river by
steel
fence posts. Water velocities were measured with a Price-Gurleytwo
current
meter. It was necessary to sample drifting benthic invertebrates because
the size of the river did not allow recovery of benthic samples during
periods of high run-off. Drift samples also provided an alternate basis
for determining biomass and production (Dimond,
Peterson, 1966).
1967;
Heaton, 1966;
Invertebrate benthos and drift samples containing invertebrates, detritus
and inorganic materials were preserved in the field with 70% ethanol.
Each sample was later separated in various ways in the laboratory. The
sample was first separated from
inorganic materials by elutrition.
were then separated from the detrital materials
using an illuminated magnifier. Further separation of invertebrates
into taxonomic groups and subsequent measurement
accomplished using
a dissecting microscope. Invertebrate organisms was
were then dried and weighed.
Invertebrate organisms
Benthic production will be calculated
by the
method proposed by Hynes and
Coleman (1968) and later modified by Hamilton (1969). In this method
production of the benthic community is estimated, rather than production
for each species. Standing crop data were converted to production
estimates by the use of size-class measurements as an index of growth
and mortality.
Allochthonous Material
In an attempt to determine the importance of allochthonous material as an
energy source for the benthic invertebrates, detrital material residual
at the time of collection of benthic samples as well as the organic
matter in drift net samples were retained for quantification.
2
These
are to be quantified by dry weight after separation into groups
according to usefulness to foraging invertebrates. Detrital materials
have been shown to serve as very important food for aquatic invertebrates
(Chapman and Demary, 1963), and a strong correlation has been demonstrated
between the abundance of detritus present and the standing crop of aquatic
insects that are not filter feeders (Egglishaw, 1964).
materials
Water Discharge and Quality
Temperature has been monitored continuously with 8-day recording thermographs on the Cedar River above and below Lake Chester Morse and at
Renton, stations 1, 3, and 6, respectively. Monitoring will be maintained
for at least two years. Temperature has been routinely measured at
Landsburg by the USGS. Discharge has been recorded at the USGS.gaging
stations above and below the reservoir, at Landsburg and Renton.
Routine measurements of water chemistry included alkalinity, dissolved
oxygen, hardness, pH, and specific conductance, determined In the field
with a Hach Laboratory Model DR-EL. A detailed anion-cation analysis
was conducted quarterly by the City of Seattle Water Quality Laboratory
according to Standard Methods (1971).
Gravel sampling was accomplished following the procedure outlined by
Koo (1964).
The method used a core-type sampler to collect gravel
samples from the stream bed. Each of three samples collected at a
station were separated into size categories using a series of variable
pore size screens and a settling cone which retained all particles smaller
than the last screen pore size. The gravel remaining In each screen after
sieving was measured by water displacement volume, including particles in
the settling cone. Sieving of the substrate of all pot samplers remaining
in the stream on the last sampling date was also completed.
RESULTS AND DISCUSSION
Tipulidae and Simuliidae
Preliminary standing crop, biomass, and estimated production of Tipulidae
and Simuliidae were calculated for the 4-mo. period September-December 1971
(Table 1) by Kittle (1972) as an undergraduate research project. The
values calculated for Simuliidae denote a substantial increase at the station
immediately below Lake Chester Morse. An increase in Simuliidae was also
noted by Spence and Hynes (1971) and Ulfstrand (1968) below a reservoir and
lake, respectively, and was attributed to the occurrence of plankton in
the outflow of these water bodies. Simuliidae feed by filtering small
particles of organic materials from the passing water and are thus able to
capitalize on an increase in small planktonic organisms made available by
a lake.
3
Table
1.
average standing crop, and average biomass of
4-mo. period (September
through December 1971) in the Cedar River.
Simuliidae
Production,
Simuliidae and Tipulidae for the
Station
Production
(mm3/m2/4-mo )
4
5
6
Biomass,
crop
(n/m2/mo)
dry weight
10,691.1
344.4
26.4
1,171,146.0
29,825.0
495,194.3
143,190.1
1134.8
67.0
1
2
3
Standing
3.1
519.3
45.9
Tipulidae
Standing crop
Stat ion
(n/m2/mo)
81.6
315.0
68.5
34.9
27.8
208.3
1
2
3
4
5
6
(g/m2/mo)
.0027
.0005
.0333
.0014
.0054
.0042
Biomass dry
(g/m: /mo)
weight
.1027
.0492
.0029
.0085
.0027
.0076
The life histories and ecology of Simuliidae have been well documented by
Maitland and Penney (1967). According to these authors Simuliidae prefer
fast-flowing areas in streams because of their method of feeding. Simullidae
attach to rocks by means of a ring of anal hooks and use a silklike thread
that they secrete as a safety line.
Larval Simuliidae undergo six instars
and may be univoltine or bivoltine.
If some of the Simuliidae obtained in
the Cedar River were bivoltine, their production was understimated.
The production of Tipulidae was not calculated because of a technical
complication in the measurement of larvae. Dr. Hynes, the originator
of the production model, has been asked to comment on the problem.
Estimates of average biomass and average standing crop have been calculated
and clearly show that the biomass was much greater at the two stations
above Lake Chester Morse than elsewhere (Table 1). According to Pritchard
and Hall (1971) Tipulidae feed on the microflora associated with decomposing
detritus in the
substrate.
Analysis of the factors in the distribution of
Tipulidae, detrital materials in the benthic samples, water quality, water
temperature,
and gravel
composition,
is incomplete but should enable us to
better understand the pattern of distribution of tipulids collected.
According to Coulson (1957) lotic aquatic Tipulidae larvae prefer fast
flowing streams with rocky bottoms and seem to be most abundant at high
altitudes. The data on Tipulidae thus far analyzed bear out Coulson's
observations; the tipulids were most abundant at the high elevations.
Although these estimates were taken from data that were collected over a
relatively short period of the year, the trends shown by them for these
two groups are expected to persist in the final analysis.
4
Other Invertebrate Groups
Confirmation of taxonomic identification for two of the major orders of
invertebrates (more than 27 species of Trichoptera and more than 20 species
of Ephemeroptera) with which we have been dealing has been received.
Specimens of a third order (Plecoptera) and a family (Chironomidae) have
been sent for identification but no confirmation has been received to date.
It is difficult to predict production estimates for invertebrate groups
other than the tipulids and simuliids or for the entire benthic community.
However, the total production of stream invertebrates is expected to be
lower at the two upper stations than at the others and slightly greater
below the dam, contrary to the findings of Lemkuhl (1972) and Spence and
Hynes (1971) because of differences in discharge regimes, and to continue
to increase at the three remaining downstream stations. The above
anticipated trend can be attributed mainly to the effects of the impoundment in the middle reach of the river and to urbanization, agricultural
run-off, and channelization in the lower reach.
Notable exceptions to
the above generalizations may occur at station 4 above Landsburg where,
because of water height, benthic sampling was restricted to the peripheral
area of the stream, and at station 5 at Cedar Grove where extensive
spawning of salmon occurred during the fall of 1971 and 1972 (Hildebrand,
1971).
The spawning activity of sockeye salmon at this station during
1972 was extensively studied, and data will be available from which the
impact of benthic invertebrate population can be inferred.
Intensive collection of data in the field was terminated in October 1972
after seventeen months. These data, when analyzed, will provide substantial
information that can be extrapolated to larger and smaller lotic systems.
Collection, sorting, and analysis of the data have taken up 3,000 hours
of work to date.of hourly employees. The necessary tasks should be
completed by September 1973, and the project completed by January 1974.
Factors Affecting Production
The previous supposition concerning the differences in production of
benthic invertebrates could be related to changes in upstream-downstream
physicochemical characteristics of the Cedar River.
These data are similar to those of Hynes (1969) inthat they show an
increase from upper to lower reaches in temperature (Figure 3), total
alkalinity (Figure 4), hardness (Figure 5), specific conductance
(Figure 6), and calcium (Appendix A) during all times of the year
with the exception of the station directly below Lake Chester Morse.
This station had very similar values to stations
and 2 above the
Lake for total alkalinity, hardness, specific conductance, and calcium
during the sampling period. The mean monthly temperature at station 3
was slightly higher than at station 1, but showed the same yearly
cycle.
Contrary to expectation, temperature regime was unlike that found
by Lemkuhl (1972) and Spence and Hynes (1971), in which temperatures
were cooler later in the spring and warmer later in the fall.
Contrary
to expectation also, the chemical factors listed above did not show
decreases at station 3 below the lake; however, the values obtained can be
explained by the discharge regime and the water exchange time of the lake.
l
5
The reservoir and lake discharge system show a regime in which epilimnetic
discharge mixes with hypolimnetic discharge.
is much smaller than Lake Chester
Masonry Pool (reservoir)
which has a water exchange
time of 0.3 yrs (Taub et al., 1972); therefore, the reservoir must have
Morse,
an extremely short water exchange time. The rapid exchange time of the
whole lake-reservoir system considered in conjunction with the discharge
of mixed hypolimnetic and epilimnetic water explains the close similarity
of station 3 to stations
and 2.
1
Dissolved oxygen (Figure 7), pH (Figure 8) and the remaining physico-
chemical data measured indicated little change related to distance downstream or proximity to the reservoir.
Some of the parameters mentioned above have been shown by researchers
to be important indicators of algal production.
Jackson (1961) found
that increased photosynthetic rates are correlated with increased total
alkalinity. Reid (1961) states that, in streams, calcium concentration
is correlated with quality and quantity of algae.
Hynes (1970) says
that low concentrations of nitrogen and phosphorus will prevail over the
length of a stream because of uptake by algae even though the amounts of
these two nutrients entering the stream may increase with distance
downstream.
Various streamside conditions may change over the course of a river and
have a marked effect on the algal production and therefore the benthic
invertebrate production, according to Hynes (1969).
Several of his
statements apply closely to the Cedar
River.
Though the upper reaches
of a stream may have very low nutrient concentration, primary production
is limited by the shading fromstreamside vegetation more than the lack
of nutrients. Farther downstream the stream becomes more turbid and
light penetration less, and these conditions together with the shading
effect will cause low primary production even though more nutrients
may be available.
On the other hand, the Cedar River is somewhat
different from that
described by Hynes since the lower reach is fairly well channelized and
streamside vegetation has been removed to a great extent. The water is
not necessarily more turbid in this reach so primary production should
be greater, especially since this reach is urbanized with some agricultural activity.
One other consideration related to benthic invertebrate production is
the species composition of streamside vegetation. As mentioned earlier,
some aquatic insects depend greatly on allocthonous detrital materials
in the stream for food. The stations above Landsburg are in primarily
coniferous forests, whereas the lower reach is bounded almost entirely
by deciduous trees. The decomposition rate of leaves is closely related
to temperature and the physical characteristics of the leaves (Kaushik
and Hynes, 1971). The lower temperatures at the upper stations associated
with the lower decomposition rate of conifer leaves (Kowal, 1969) will
increase decomposition time, and more of this detrital material will be
exported to lower stream areas.
Conversely, the lower river has higher
temperatures and more rapidly decomposing leaves (Kaushik and Hynes,
1971).
The effect of these different types of leaves and decomposition
rates will depend on the volume of the materails, the trophic structure,
and species composition of the different stream areas.
6
Contour maps of the six sampling stations were prepared by the use of
the Symap Contour Plot of Three Dimensional Surfaces, University of
Washington Fisheries Research Institute, program number FRB 726, from
which depth areas will be determined.
The gravel samples collected (Table 2) indicated some rather large
differences in the substrate at the six stations as well as some even
larger differences between pot contents and gravel samples at
four of the stations where pot samplers were used. The differences
between gravel samples at the station varied from 0.7 to 28.0 per
cent for all size categories. The differences between the insect
samplers at the stations varied from 0.6 to 35.6 per cent for all
size categories. These differences do not illustrate the larger
differences between the results obtained with the gravel sampler
and those obtained with the insect sampler. The difference between
these two is better illustrated by the mean percentage of each gravel
size as seen in Table 2. The largest size class of gravel was over
represented in the.insect sampler. The next two smaller size classes
were approximately equal in percentage composition; however, the
remaining seven categories were all underrepresented in the insect
sampler except the 0.841 mm size group,which was overrepresented in
the insect sampler. These variations are partially explained by
the size of the gravel sampler, which was only 6 inches in diameter
and could be used only where the largest particles in the substrate
did not exceed the diameter of the sampler. It can be seen that
the gravel sampler was biased toward smaller particle sizes. The
pot samplers were probably biased toward larger particle sizes
because of the size of the openings in the container material,
which allowed passage of particles smaller than 13 mm, together
with the fact that each time a pot was sampled for insects all
particles smaller than 7 mm were removed in the sampling procedure.
The material removed was replaced from surrounding materials; however,
with continuous sampling the larger particles probably increased in
percentage.
Table 2.
Station
no.
1
1
Average percentage gravel composition of stream substrate at the six Cedar River station
sieve size
Type of
(mm)
sample
collection
26.9
13.5
6.73
3.36
1.68
.841
.420
.210
.105
LT. 105
Gravel sampler
41.1
13.1
8.6
6.4
6.1
9.1
8.6
3.2
1.3
2.5
56.8
18.2
9.6
0.7
0.7
7.5
2.5
0.6
0.7
2.2
Insect samper
(pot)
2
Gravel sampler
41.9
14.5
10.0
8.9
7.7
5.9
3.6
1.9
1.1
3.9
2
Insect sampler
67.9
12.0
9.0
3.1
0.2
2.5
1.6
0.7
0.4
2.0
3
Gravel sampler
29.3
14.0
13.9
12.0
10.9
6.6
3.7
1.8
1.1
6.1
3
insect sampler
42.1
12.0
8.1
2.0
0.0
34.7
0.1
0.1
0.1
0.5
4
Gravel sampler
13.9
17.0
13.6
10.8
11.4
11.6
12.9
6.1
1.0
1.4
4
Insect sampler
32.3
17.0
10.1
1.5
0.0
33.1
2.1
2.0
0.4
1.1
5
Gravel sampler
26.8
15.7
15.4
11.7
8.9
9.6
7.5
2.3
1.4
0.2
5
Insect sampler
-
-
-
-
-
-
6
Gravel sampler
29.5
12.5
10.8
9.6
8.4
8.0
5.4
1.7
2.9
6
Insect sampler
-
mean
Gravel sampler
30.4
14.4
12.0
9.9
8.9
8.4
7.8
3.4
1.2
2.8
mean
Insect sampler
49.7
14.8
9.2
1.8
0.2
19.4
1.5
0.8
0.4
1.4
-
-
-
10.9
-
LITERATURE CITED
Standard methods for the
1971.
AMERICAN PUBLIC HEALTH SERVICE.
769 p.
New York.
13th ed.
of water and waste water.
examination
1963. Seasonal changes in the food ingested
D. W., and R. DEMARY.
by aquatic insect larvae and nymphs in two Oregon streams. Ecol.
CHAPMAN,
44:140-146.
COLEMAN,
M. J., and H. B. N. HYNES.
1970.
the invertebrate fauna in the bed of a
The vertical distribution
Limnol. Oceanog.
stream.
of
15:31-40.
J. C.
COULSON,
Reserve.
Observations on the Tipulidae of the Moor House
Ent. Soc. London 111:157-174.
1957.
Trans.
DIMOND, J. B.
Roy.
1967.
Evidence that drift of stream benthos is
density
Ecology 48:855-857.
related.
1964. The distributional relationship between the
bottom fauna and plant detritus in streams. J. Animal. Ecol.
EGGLISHAW, H. J.
33:463-476.
HAMILTON, A. L.
14:771-782.
HEATON,
J. R.
On estimating annual production.
1969.
1966.
Limnol. Oceanog.
The benthos and drifting fauna of a riffle in the
Madison River, Yellowstone National Park.
Ph.D. Thesis.
Montana
State University.
1971. The effect of coho spawning on the benthic
invertebrates of the Platte River, Benzie County, Michigan. Trans.
Amer. Fish. Soc. 100(1):61-68.
HILDEBRAND, STEPHEN G.
IN:
B. N.
1969. The enrichment of streams, p. 188-196.
Causes, consequences, correctives. National
Eutrophication:
Academy of Sciences, Washington, D.C.
HYNES, H.
HYNES, H. B.
N.
1970. The ecology
555 P.
of running waters.
Univ. Toronto
Press, Toronto.
1968. A simple method of assessing
M. J. COLEMAN.
the annual production of stream benthos. Limnol. Oceanog. 13:569-573.
HYNES, H. B. N., and
JACKSON, D. F.
1961.
Comparative studies of
in relation to total
alkalinity.
Verh.
phytoplankton
Internat.
photosynthesis
Verein. Limnol.
14:125-133.
The fate of the
1971.
N. HYNES.
68:465-515.
Arch.
Hydrobiol.
streams.
KAUSHIK, N. K., and H.
that fall into
B.
9
dead leaves
KOO, T. S. Y. [ed.]
1964.
College of Fisheries,
FRI Field Manual.
Fisheries
Univ. Washington. Circular
No.
Research Institute,
143 (revised edition).
1972. An estimation of Tipulidae and Simuliidae
production in the Cedar River. M.S. research paper, Fish.
Inst.
12 p. (Typewritten).
KITTLE, LEWEY J. Jr.
(Diptera)
Res.
KOWAL, N. E.
LEHMKUHL,
Effect of leaching on pine litter decomposition
1969.
Ecol.
rate.
D. M.
50:739-740.
1972.
Change in thermal regime as a cause of reduction
of benthic fauna downstream of a reservoir.
Canada 29:1329-1332.
J. Fish.
Res. Bd.
MAITLAND, P. S., and MARGARET M. PENNEY.
1967.
The ecology
in a Scottish river. J. Animal Ecol. 36:179-206.
MILLER, D.
1961.
A
modification
of the
simultaneous high-speed plankton
of Simuliidae
small hardy plankton sampler for
Bull. Mar. Ecol.
hauls.
5(45):165-172.
PETERSON, G. R.
1966.
The relationship of invertebrate drift abundance
to the standing crop of benthic organisms in a small stream. M.S.
Thesis.
University of British Columbia.
PRITCHARD,
G., and
H. A. HALL.
1971.
An introduction to the biology of
craneflies in a series of abandoned beaver ponds with an account
of the life cycle of Tipula sacra Alexander (Diptera; Tipulidae).
Canad. J. Zoo). 49(4):467-482.
REID, G. K.
1961.
Ecology of inland waters
Book Corporation, New York.
375 P.
SPENCE, J. A.,
and H. B. N.
HYNES.
upstream and downstream of an
.1971.
and estuaries.
Reinhold
Differences in benthos
impoundment.
J. Fish.
Res. Bd.
Canada 28:35-43.
SURBER, E. W.
1937.
Rainbow trout and bottom fauna production
mile of stream. Trans. Am. Fish. Soc. 66:193-202.
in one
ULFSTRAND, S.
Life cycles of benthic .insects in Lapland streams
1968
(Ephemeroptera, Plecoptera, Trichoptera, Diptera, Simuliidae).
Oikos 19:156-190.
10
(
L
'-"-——WAIER SHED BOUNDARY
,—•'
DIVERSION
#7Th
DAM
1—6
SAMPLING STATION
Fiqure 1.
Map of the Cedar River basin showinq samplinq stations.
POT SAMPLER
BEING LIFTED
EXPANDED STEEL MESH
f- .5 in ...*.
POT SAMPLER IN SITU
Figure
2.
DeSIgn of pot
sampler,
adapted from Coleman and Hynes
(1970).
. STATION
3
J
0
0 ONDJFMAMJJASON
ONDJFMAMJJASON
STATION
0
Fiqure 3.
6
ONDJ FMAMJJASON
Monthly mean temperatures at samplinq stations 1, 3, and 6,
immediately above and below Lake Chester Morse and at Renton, respectively.
40-1
STATION 1
STATION 2
20-
\
OLIN
, M,
\\\\
1
1,
\
\
\
0
40-;1
STATION 3
STATION 4
r
11
0
40-
STATION 5
STATION 6
I
L
20
14
0
N faVNN
^NMNNfVN
0-Gov. ON NO -iwcoODM0
1971
Fiqure
4.
t
Total
1372
CO
M
NN
N
N
N
p A lO OI C1971
.- O)MN NM NN
N NNNNN
N
N N 7 7 tO tD n m TO
1
1972
alkalinity at all stations and monthly sampling periods.
STATION
40
1
20-
14
STATION 3
40-
I
I
ppm 20-
0
40-
STATION 6
STATION 5
IN
11
0
N M Z 4 N YI P ^ NMN N N N
tOtiWOf O_ N NO OW<D W° 2
1%71 Y '
Figure 5.
1372
Hardness (CaCO3)
\
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N-RM
MNCI
N
fV
N
NNN
16 h4a O NON 740" W0/e
co
OM9 N
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1971
1
1972.
at all stations and monthly sampling periods.
STATION 2
STATION I
80-1
40-
I
0
80-
STATION 3
STATION 4
STATION 5
STATION 6
0
80-
.16
40'
,
\\\
0
N N N N N^ N H N N N
forno'cVV V aowo omo
1971
Figure 6.
I
1972
NNN'N'NM
NNNN
0,0 "
tD a1 ON Nom' 44D 10 CD 01 O
1971
I
1972
Specific conductance at all stations and mcnthly sampling periods.
STh,TION 1
20
0
M
10
0
STATION 3
I
ppm 10
0
STATION 5
20
STATION 6
si
I
10
,"I
0
r-c%NfHt Y)R-A.. NRnN
4010)01 O N NO.-row 1
1971
Figure 7.
034M
1372
Dissolved oxygen
sampling periods.
NNNU Nv}N Am ANC'1N
NNNNN
10 rQ! 0 NNY44QLnW010
7
1971
^I
1972
concentrations at all stations
and monthly
STATION 2
6
STATION 3
S TAT ION 4
STATION 5
STATION 6
6
8
Q
\\\i
\\
\
\\I
1
7
6
N HfVN(VNMCVNNNN
CO fPY
mnWmON NO Q<O S0 10000
,0 nO/0f
.971
Figure 8.
1372
pH at all sampling stations and
N NN
!100)
CV
N
0)(')ANf'1NN NNNNN
NN O 4w,,
197-'.'1
Of6
1972
monthly sampling periods.
APPENDIX A
Data on water quality at the six Cedar River stations as measured by the
City of Seattle Water Quality Laboratory
28 June 1971
Station number
Chemical factor
3
4
5
6
14.0
12.5
13.5
1.9
1.3
3.0
1.6
1.5
1
7.0
6.5
Free CO2 (ppm)
2.6
2.2
8.0
2.4
Chloride (ppm)
1.1
1.5
1.4
Chromium (ppm)
BDL*
BDL
BDL
BDL
BDL
BDL
Copper (ppm)
< .01
< .01
< .01
< .01
< .01
< .01
Fluoride (ppm)
<
.1
< .1
<
<
Hardness
(CaC03) (PPm)
10.0
11.6
19.0
19.0
Calcium
(mg/1)
.1
.1
<
<
9.4
Iron (ppm)
.05
.06
Lead (ppm)
< .005
< .005
.005
.1
18.0
.15
.10
.06
.05
<
.1
8
< .005
< .005
1.2
1.6
1.1
.02
< .02
< .02
< .005
Magnesium (ppm)
0.7
0.7
0.9
Manganese (ppm)
< .02
< .02
< .02
.01
.01
.01
.01
.01
.05
.05
.05
.05
.05
.01
.03
.01
.015
.01
<
Nitrogen (ppm)
.015
.05
Ammonia
Nitrate
Nitrite
-
Organic
Phosphate (ppm)
BDL
BDL
BDL
BDL
BDL
BDL
35
6
29
35
30
2
17
28
28
29
3
6
8
8
28
14
17
22
20
22
21
Potassium (ppm)
Residue (mg/1)
Total
Filterable
Nonfilterable
Fixed
Silica
(mg/1)
Sodium
(mg/1)
Sulfate (mg/1)
Surfactants (mg/1)
Tannin-lignin (mg/1)
Physical analysis
Color units
Turbidity (JTU)
25
26
26
8.5
8.5
8.5
8.5
9.6
9.6
1.2
1.7
1.1
1.1
1.7
1.1
BDL
BDL
.09
10
0.25
BDL
.05
.01
10.5
11
0.20
*BDL - Below Detectable Limits
19
BDL
0.25
.01
11
.0.30
BDL
BDL
< .01
< .01
8
0.70
11
1.10
APPENDIX A
Data on water quality at the six Cedar River stations as measured by the
City of Seattle Water Quality Laboratory
12 July 1971
Chemical factor
Station number
2
3
4
5
6
18.5
19.0
6.5
6.0
8.0
16.0
Free CO2 (ppm)
3.4
2.5
1.1
1.5
-
-
Chloride (ppm)
.8
1.0
1.0
1.1
1.1
1.5
Chromium (ppm)
BDL*
BDL
BDL
BDL
Copper (ppm)
< .01
< .01
< .01
< .01
Fluoride (ppm)
< .1
<
Calcium
(mg/i)
Hardness
(CaC03) (PPm)
8.5
.1
Iron (ppm)
< .1
<
10.0
21.0
22.0
.23
.09
BDL
02
.03
.1
<
8.5
.07
BDL
.1
.1
<
24.5
.10
.09
.15
-
-
-
-
-
Magnesium (ppm)
0.5
0.6
0.5
1.2
0.9
1.3
Manganese (ppm)
0.0
0.0
0.0
0.0
0.0
0.0
0.0
< .05
0.0
< .05
0.0
< .05
0.0
0.0
0.0
< .05
< .05
< .05
Lead (ppm)
Nitrogen (ppm)
Ammonia
Nitrate
Nitrite
Organic
-
-
-
-
-
-
0.12
0.30
0.25
0.27
0.55
0.36
Phosphate (ppm)
.02
.01
.01
.01
.02
.05
Potassium (ppm)
.17
.17
.08
.17
.25
.25
Residue (mg/1)
Total
42
47
Filterable
6
36
7
Nonfilterable
Fixed
50
9
40
69
6
63
41
-
-
-
60
77
5
72
5
55
-
-
-
Silica
(mg/1)
6.6
9.6
8.0
10.7
8.3
11.5
Sodium
(mg/1)
1.1
1.4
1.2
1.6
2.5
2.5
Sulfate (mg/1)
1.0
0.8
1.0
1.1
1.1
1.1
Surfactants (mg/1)
Tannin-lignin (mg/1)
Physical analysis
BDL
BDL
BDL
.32
.09
BDL
.12
BDL
.07
.09
Color units
5
5
5
5
5
Turbidity (JTU)
0.3
0.25
0.3
0.2
0.25
*BDL - Below Detectable Limits
20
BDL
.09
12
0.6
APPENDIX A
Data on water quality at the six Cedar River stations as measured by the
City of Seattle Water Quality Laboratory
25 September 1971
Chemical factor
Calcium
(mg/1)
Station number
1
2
11.5
10.0
3
9.0
Free C02 (ppm)
-
-
-
Chloride (ppm)
1.3
1.2
1.2
Chromium (ppm)
-
4
5
19.5
18.5
19.0
-
1.2
1.3
1.5
-
-
Copper (ppm)
<0.01
<0.01
<0.01'
<0.01
<0.01
<0.01
Fluoride (ppm)
<0.1
<0.1
<0.1
<0.1
<0.1
<O.1
11.8
12.6
10.2
24.0
22.4
25.2
Hardness
(CaC03) (ppm)
Iron (ppm)
.09
< .005
Lead (ppm)
.18
.14
< .005
.23
< .005
< .005
1.2
4.5
.35
< .005
.22
< .005
Magnesium (ppm).
.3
Manganese (ppm)
-
Nitrogen (ppm)
Ammonia
.028
.o16
.015
.009
.007
.012
.032
.09
-
-
.09
.10
<0.01
<0.01
<0.01
<0.01
6.6
10.6
10.2
12.0
1.1
1.6
1.4
1.8
2.6
3.9
1.5
-
Nitrate
Nitrite
Organic
<0.01
Phosphate (ppm)
<0.01
-
Potassium (ppm)
Residue (mg/1)
Total
Filterable
Nonfilterable
Fixed
Silica
(mg/1)
9.8
Sodium
(mg/1)
-
-
2.8
1.2
Sulfate (mg/1)
Surfactants
(mg/1)
Tann i n -li gn n
i
(
mg /1)
.025
.
04
12.0
.
BDL
BDL
BDL*
26
.
Physical analysis
Color units
Turbidity (JTU)
*BDL - Below Detectable Limits
21
04
.
04
.01
.01
.04
.10
APPENDIX A
Data on water quality at the six Cedar River stations as measured by the
City of Seattle Water Quality Laboratory
i April 1972
Station number
Chemical factor
Calcium
2
7.4
5.4
6.2
(mg/ 1)
3
4
5
6
12.6
1.30
17.0
BDL
BDL
BDL
< .01
<
Free C02 (ppm)
Chloride (ppm)
Chromium (ppm)
BDL*
Copper (ppm)
<
.01
BDL
BDL
<
.01
<
.01
Fluoride (ppm)
0.1
0.15
0.1
Hardness
(CaCO3) (PPm)
7.8
6.1
7.8
.125
Iron (ppm)
0.1
15.3
.01
< .01
0.15
0.1
17.2
22.4
.87
.32
.97
.21
Lead (ppm)
Magnesium (ppm)
Manganese (ppm)
Nitrogen (ppm)
Ammonia
Nitrate
Nitrite
Organic
Phosphate (ppm)
.01
<
<
.01
.01
<
.01
<
.01
<
.01
Potassium (ppm)
Residue (mg/1)
Total
Filterable
Nonfilterable
Fixed
Silica
(mg/1)
Sodium
(mg/1)
Sulfate (mg/1)
Surfactants (mg/1)
Tannin-lignin (mg/1)
Physical analysis
Color units
0.6
0.6
0.6
0.7
0.17
0.56
0.15
0.07
Turbidity (JTU)
*BDL - Below Detectable Limits
22
0.9
1.3
APPENDIX A
Data on water quality at the six Cedar River stations as measured by the
City of Seattle Water Quality Laboratory
November 10, 1972
Chemical factor
Station number
3
1
Calcium
9.6
(mg/1)
-
Free CO2 (PPm)
Chloride (ppm)
Chromium (ppm)
0.95
.005
(BDL*)<
8.0
-
8.0
0.85
0.9
4
5
6
22.8
18.6
27.2
-
-
1.1
-
1.25
1.65
< .005
< .005
< .005
< .005
< .005
Copper (ppm)
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
Fluoride (ppm)
<0.1
<0.1
<0.1
<0.1
<0.1
<0.1
9.6
9.0
9.0
26.2
24.6
34.4
(ppm)
0.025
0.065
0.07
Lead (ppm)
<0.005
<0.005
0.0
1.0
Hardness
(CaC03)
Iron
(PPm)
Magnesium (ppm)
Manganese (ppm)
0.065
0.065
0.14
<0.005
<0.005
<0.005
<0.005
1.0
3.4
6.0
7.4
BDL
BDL
BDL
BDL
<0.05
<0.05
<0.05
<0.05
0.1
0.1
-
-
<0.01
<0.01
<0.01
<0.01
0.01
0.025
4.3
6.1
6.6
7.1
**
**
**
BDL
BDL
Nitrogen (ppm)
Ammonia
Nitrate
Nitrite
Organic
Phosphate (ppm)
Potassium (ppm)
Residue (mg/1)
Total
-
Filterable
Nonfilterable
Fixed
Silica
(mg/1)
Sodium
(mg/ 1)
-
-
4.7
6.1
**
Sulfate (mg/1)
Surfactants (mg/1)
Tannin-lignin (mg/1)
BDL
Physical analysis
Color units
Turbidity (JTU)
10
0.3
0.3
**
**
BDL
BDL
0.8
12
0.6
*BDL - Below Detectable Limits
BDL
0.4
0.25
5
8
0.55
0.45
BDL
0.3
10
0.5
BDL
0.3
10
0.6
**Due to difficulty of precision using the BaCl turbid metric method, no
accurate data was obtained. However, all stations were certainly <3mg/l.
23