EPA-600/2-76-262
September 1976
Environmental Protection Technology Series
EFFECTS OF LOG HANDLING AND
STORAGE ON WATER QUALITY
Industrial Environmental Research Laboratory
Office of Research and Development
U.S. Environmental Protection Agency
Cincinnati, Ohio 45268
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U.S. 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.
This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia 22161.
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EPA-600/2-76-262
September 1976
EFFECTS OF LOG HANDLING AND STORAGE ON WATER QUALITY
By
Gerald S. Schuytema
Robert D. Shankland
Food and Wood Products Branch
Industrial Environmental Research Laboratory
Corvallis, Oregon 97330
Contract No. 12-100 EBG
Project Officer
H. Kirk Willard
Food and Wood Products Branch
Industrial Environmental Research Laboratory
Corvallis, Oregon 97330
INDUSTRIAL ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
CINCINNATI, OHIO 45268
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DISCLAIMER
This report has been reviewed by the Industrial Environmental
Research Laboratory-Cincinnati, U.S. Environmental Protection Agency,
and approved for publication. Mention of trade names or commercial
products does not constitute endorsement or recommendation for use.
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FOREWORD
When energy and material resources are extracted, processed,
converted, and used, the related pollutional impacts on our en-
vironment and even on our health often require that new and in-
creasingly more efficient pollution control methods be used. The
Industrial Environment Research Laboratory - Cincinnati (lERL-Cl)
assists in developing and demonstrating new and improved methodo-
logies that will meet these needs both efficiently and economical-
ly.
This report reviews the biological and chemical effects of
three types of log storage on water quality. This study was a
part of the general EPA research program to determine the effects
of all industrial and agriculture activities on water quality and
was undertaken because there was little information available on
the effects of logging.
The report also identifies the problems associated with log
storage and provides facts upon which to base regulations control-
ling log storage to minimize environmental impact. The report can
be used by state and federal regulatory agencies and will also be
of interest to industries involved in log storage and handling.
For further information please contact the Food and Wood Products
Branch of the Industrial Environmental Research Laboratory,
Cincinnati.
David G. Stephen
Director
Industrial Environmental Research Laboratory
Cincinnati
iii
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ABSTRACT
The biological and chemical effects of three types of
log storage on water quality were investigated. Three flow-
through log ponds, two wet deck operations, and five log rafting
areas were studied. Both biological and chemical aspects of
stream quality can be adversely affected by flow-through log
ponds and runoff from wet decks. Severity of degradation varies
widely with each situation. Runoff from wet decks had pollution
characteristics equal to or greater than that of the waters
from the flow-through log ponds studied.
Esthetically, a stream can be affected by the dark color
of the water coming from a log pond or wet deck. Floating
bark from a log raft or a log pond is also aesthetically dis-
pleasing. The most significant problem associated with log
rafting is the loss of bark which commonly occurs when the logs
are dumped into the water.
This report was submitted by the Food and Wood Products
Branch, Con/all is Field Station, Industrial Environmental Research
Laboratory-Cincinnati under the sponsorship of the Environmental
Protection Agency. Work was completed as of June 1974.
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CONTENTS
Page
Sections
I Conclusions 1
II Recommendations 2
III Introduction 3
IV Selection of Study Sites 9
V Methods of Sample Collection and Analysis 10
VI Results 14
Lobster Creek 14
Elk Creek 20
Row River 25
Middle Fork of the John Day River 33
Steamboat Slough 42
Elochoman and Cathlamet Sloughs 47
Coal Creek Slough 54
Multnomah Channel 60
Siuslaw River 65
VII References 73
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TABLES
Page
No.
1. Lobster Creek Study Site Bottom-Dwelling Organisms 16
2. Lobster Creek Study Site Water Chemistry Data 18
3. Elk Creek Study Site Bottom-Dwelling Organisms 21
H. Elk Creek Study Site Water Chemistry Data 22
5. Row River Study Site Water Chemistry Data 28
6. Row River Study Site Bottom*Dwelling Organisms 30
7. Sampling Stations Middle Fork John Day River Study Site 35
8- Middle Fork of the John Day River Study Site Water 36
Chemistry Data
9. Middle Fork of the John Day River Study Site Bottom- 37
Dwelling Organisms
10. Steamboat Slough Study Site Bottom-Dwelling Organisms 44
11. Steamboat Slough Study Site Water Chemistry Data 46
12. Sampling Stations Elochoman and Cathlamet Sloughs 50
Study Site
13. Elochoman and Cathlamet Sloughs Study Site Bottom- 51
Dwelling Organisms
14. Elochoman and Cathlamet Slough Study Site Water 52
Chemistry Data
15. Sampling Stations Coal Creek Slough Study Site 56
16. Coal Creek Slough Study Site Bottom-Dwelling Organisms 58
17. Coal Creek Slough Study Site Water Chemistry Data 59
18. Multnomah Channel Study Site Bottom-Dwelling Organisms 62
19. Multnomah Channel Study Site Water Chemistry Data 64
20. Sampling Stations Siuslaw River Study Site 67
21. Siuslaw River Study Site Bottom-Dwelling Organisms 69
22. Siuslaw River Study Site Water Chemistry Data 70
VI
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FIGURES
Page
NO.
1. Lobster Creek Study Site ^
2. Elk creek Study Site 23
3. Row River Study Site *•'
H. Middle Fork John Day River Study Site 38
5. Steamboat Slough Study Site 43
6. Elochoman and Cathlamet Sloughs Study Site 48
7. Coal Creek Slough Study Site 55
8. Multnomah Channel Study Site 61
9. Siuslaw River Study Site 66
VII
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ACKNOWLEDGEMENT
The cooperation and assistance of the various companies involved
in this study, the Oregon Department of Environmental Quality,
and the Washington State Department of Ecology is gratefully
acknowledged.
Appreciation is expressed to Thomas Hamlin, Donald Hatler,
Charles Politykar and Richard Whitmer for their assistance in the
tedious task of sorting also identifying the biological organisms
collected during this study, and Alvin L. Ewing, and Mark E.
McElroy, Industrial Wastes Branch, for assistance in preparing
this report for publication.
viii
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SECTION I
CONCLUSIONS
1. Dissolved oxygen in flow-through log ponds tends ,to become
depleted during summer months when flows are low and the
waters are warm.
2. Both biological and chemical aspects of water quality can be
adversely affected by flow-through log ponds.
3. The discharge from flow-through log ponds is esthetically
displeasing, due mainly to the dark color of the water.
This dark color persists downstream until it is diluted out.
4. The runoff from wet decks has pollutional characteristics
equal to or greater than that of waters from flow-through
log ponds.
5. While wet deck runoff has the potential to degrade water
quality in a receiving stream, especially under low flow
conditions, this effect could not be directly demonstrated.
6. The effects of handling and rafting logs on water quality in
rivers and sloughs depends on the intensity of such activity
and the stream's flushing action. A signficant problem
associated with water storage is the loss of bark during log
dumping. Degradation will tend to be greater when larger
amounts of logs are handled and rafted. Flushing action of
the stream may reduce degradation, or even transfer the
problem to another area.
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SECTION II
RECOMMENDATIONS
Each situation is unique, but the following recommendations
should be helpful in establishing guidelines for individual
situations.
1. The use of flow-through type log ponds should be
discouraged.
2. Where it is not practical to eliminate flow-through ponds
certain minimum requirements should be met to protect
downstream water quality.
a. Downstream water uses should not be adversely affected
by the discharge from the log pond.
b. The log pond should not be located on a stream used
for valuable fish production, especially migratory
fish.
c. Some method of aerating the discharge from the log
pond should be provided. This might include the use
of an aerator near the point of discharge, or having
turbulent flow over the spillway.
3. When it is necessary to drain a log pond for cleaning, or
repair, adequate precautions should be taken to protect
downstream water quality. At many sites spray irrigation
onto the land would possibly be a suitable means of
disposing of the water. If spray irrigation is not
feasible, then cleaning should take place during a period of
high flow to minimize the impact on water quality.
4. Flow-through type log ponds should be cleaned periodically
to remove accumulated bark and other organic debris.
Precautions should be taken at all times to prevent floating
debris from escaping.
5. Runoff from wet decks should not be discharged directly to
the receiving water. Three possible ways of handling wet
deck runoff are: collection and reuse of the runoff for
sprinkling; spray irrigation if adequate land is available;
containment in shallow basins to allow natural evaporation.
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SECTION III
INTRODUCTION
The research* described in this report was intended to determine
the effects of various methods of log handling and storage on
quality of receiving waters. Both the biology and chemistry of
the receiving waters were evaluated with emphasis on biology.
In many areas the supply of logs to processing mills may be
seasonal due to climatic conditions, making it necessary to store
logs in order to maintain production throughout the year. Rapid
harvest of trees because of disease, forest fire damage, or other
reasons may result in an excess of logs that must be stored until
they can be processed. Fluctuations in the price of timber and
market for lumber can likewise significantly influence the
amount of logs in storage.
A major consideration in long-term storage of logs is maintenance
of their quality. Checking, insect damage, and infestation by
fungi are all of concern. If logs are allowed to dry out they
tend to split, or check. In addition to decreasing the value of
the logs, the checks offer entryway for attack by insects and
fungi. In some parts of the country, severe checking may occur
after only a few months of storage if preventive measures are not
taken (Dobie 1965). The most common method of preventing or
minimizing checking is keeping the logs wet.
McHugh et al. (1964) report that there are about 4,860 ha (12,000
ac) of log ponds and 800 ha (2,000 ac) of sloughs or canals used
as log ponds in Oregon. In addition, there are about 1,620 ha
(4,000 ac) of log ponds in Washington, 1,620 ha (4,000 ac) in
northern California, and 400 ha (1,000 ac) in Idaho. The size of
the ponds varied from less than a hectare to over 160 ha (400
ac). Water depths ranged from 1 to 9 meters.
TiWhen this research was conducted, Gerald S. Schuytema was in the Laboratory
Services Branch; he is now with the Eutrophication and Lake Restoration Branch
of the Pacific Northwest Environmental Research Laboratory. Robert D. Shankland
is now with the Enforcement Division, Denver Regional Office, EPA.
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Prior to 1968 little work had been done on determining the
influence of various log handling and storage practices on water
quality. Probably the most extensive work on the subject up to
then had been done by McHugh et al. (1964). Although the major
emphasis of their study was directed toward mosquito problems
associated with log ponds, water quality analyses were made on
waters from over 80 ponds. In 1968 Oregon State University began
extensive studies on the influences of log handling and storage
practices of water quality. These studies, under the supervision
of Dr. Frank Schaumburg, were financed in part by EPA Research
Grant EPA-R2-73-085.
The chemistry of wood is complex, involving many different
organic compounds. Browning (1963) grouped the constituents of
wood into the following classifications: carbohydrates, phenolic
substances, terpenes, aliphatic acids, alcohol, proteins, and
inorganic substances. The relative amounts of the various
compounds varies with such factors as the species and age of the
wood. The carbohydrates consist mainly of polysaccharides, which
include cellulose, hemicelluloses, starch, pectic substances, and
arabinogalactans. Wood is approximately 75 percent
polysaccharides, about three-quarters of which is cellulose.
Wood is relatively insoluble (roughly one percent by weight) in
cold water. The percentage entering solution increases with
temperature, which is largely attributed to increased hydrolysis
(Browning 1963) .
The chemistry of bark differs somewhat from that of wood, with
one of the differences being the amounts of extractives obtained
(Browning, 1963). Generally bark has a higher percentage of
material extractable in hot water than does wood. These include
tannins, simple sugars, glycosides, polysaccharides, gums, and
pectins.
Graham and Miller (1969) and Schaumburg (1970) found that
significantly greater quantities of organics were leached from
ponderosa pine logs than from Douglas-fir logs. This might be
expected based on the relative amounts of hot water extractable
material that have been reported for the two barks (Browning
1963);ponderosa pine 12.1 percent, Douglas-fir 2.3 percent.
Schaumburg (1970) found bark to be the main source of color
producing compounds leached from the logs, as measured by the
Pearl-Benson Index (PBI).
McHugh, et al. (1964) made similar observations concerning bark
as the main source of color producing compounds in log pond
waters. Leaching rates were found to be concentration dependent,
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with the rates tending to decrease as the concentration of
organics in the holding water increase. In fresh flowing water
the rate of leaching is likely to be relatively consistent for
periods up to 80 days or more.
Ninety-six-hour bioassay studies (Schaumburg 1970) were conducted
to determine the toxicity of leachates from Douglas-fir, hemlock,
and ponderosa pine logs to chinook salmon and rainbow trout fry.
There were no mortalities to trout fry in 100 percent solutions
of leachate from ponderosa pine and older (120 years) Douglas-fir
logs. Similarly, there were no mortalities to salmon fry in 100
percent solution of leachate from hemlock. Leachate from
younger (50 years) Douglas-fir logs was somewhat toxic to salmon
fry. The leachate from log segments without bark tended to be
more toxic than the leachate from log segments with bark.
Oxygen uptake rates of benthic (bottom) deposits of bark were
studied by Neal and preliminary results of part of his work have
been reported (Schaumburg 1970). A specially designed benthic
respirometer was used for in situ determinations of oxygen uptake
rates in a fresh flowing stream storing ponderosa pine logs. In
a control area, the oxygen uptake rate was 0.19 gO?/m /day, while
at three stations with bark, the rates ranged from 0.38 to 2.09 ^
/mz/day. The volatile solids content of the top 5.1 cm of the
benthic deposits ranged from 8.1 to 86.5 kg/m3. The oxygen
uptake rate increased with increasing volatile solids content.
Stein and Denison (1966) observed an in situ uptake rate of about
3.6 gQ2/m2/day for a cellulose sludge deposit as compared to 1.1
gO2/mVday for a sandy bottom. Based on laboratory studies of
paper and a paperboard mill sludge, McKeown et al. (1968)
concluded that the oxygen uptake rate does not increase at sludge
depths greater than 0.3 m. They also concluded that the oxygen
demand is increased by mixing or turbulence.
Schaumburg (1970) made hypothetical calculations on the bark
loss, benthic oxygen uptake, and leached organics associated with
ponderosa pine logs. He calculated that about 213,600 kg of bark
(dry weight basis) would be dislodged from 37,100 m3 of logs
during unloading (vertical dumping) and 30 day raft storage.
About 147,000 kg of the bark would have sunk by the end of the 30
day storage period. The benthic oxygen demand of 20 ha(50 ac) of
sunken bark, was calculated to be 100.7 kg of 0^ /day. A storage
area of 20 ha (50 ac) hypothesized to be covered with logs for 30
days, was calculated to contribute daily a COD of 317 kg and a
BOD of 145 kg. Chemical oxygen demand (COD) is a measure of the
amount of oxygen needed to chemically oxidize most organic
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compounds. Biochemical oxygen demand (BOD) is the quantity of
oxygen used in the biochemical oxidation of organic matter at a
specified time and temperature, normally 5 days and 20°C. The
authors pointed out that the significance of the pollutants
attributable to log rafts must be evaluated for each individual
circumstance.
There are few specific studies on biological problems associated
with log handling and storage practices in the Pacific Northwest.
Numerous investigations have demonstrated the harmful effects of
wood fiber discharged to a stream (Bartsch 1949, Bartsch 1960,
Ellis 1943, Westfall 1946). The blanketing action of these
fibers decreases productivity by smothering aquatic organisms and
covering fish spawning beds. Decomposition of the matted fibers
also uses up dissolved oxygen necessary to a desirable aquatic
community, in addition to being unsightly.
Log storage debris and wood chips were among the wastes believed
detrimental to the aquatic life of the Yaquina River and Bay,
Oregon (USDI 1968). Bark and debris from log rafting were
harmful to dungeness crab habitats in Hamilton Bay, Alaska
(McHugh 1968). The crab were not found within areas heavily
covered by bark but were abundant outside of these areas.
Accumulated bark from stream driven pulpwood in New Brunswick,
Canada, depleted dissolved oxygen to 12 to 65 percent below
saturation (Wright 1963). These accumulations remain on the
bottom for long periods and represent a constant danger to fish
populations.
SIGNIFICANCE OF BIOLOGICAL STUDIES
The response of aquatic plants and animals to a polluted
environment have been discussed by numerous authors(Hynes 1960,
Ingram 1960, Keup 1960, Klein 1962, Mackenthun 1969). Elements
of the biota that are commonly studied include the bottom
dwelling animals, attached algae and slime organisms.
Bottom Dwelling Animals
The kinds and numbers of bottom-dwelling animals inhabiting a
particular stream reflect the quality of water that has generally
prevailed in the area for an extended period of time. Some of
these animals are capable of withstanding polluted conditions,
and increase rapidly in population when competition with other
forms is eliminated. Examples of some animals which can
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withstand organic pollution are sludgeworms, certain midge
larvae, leeches and lung-breathing snails. As conditions
suitable for these tolerant organisms develop, the more sensitive
animals such as stoneflies, mayflies and caddisflies are removed
from the community. Ultimately, a population consisting of large
numbers of only one or two species can make up the fauna of a
stream bottom. A bottom-dwelling population consisting of small
numbers of a large variety of organisms is typical of the
unpolluted habitat. Although some of the pollution tolerant
forms would form part of such a community, they would be in the
minority.
When a single species dominates the population to the exclusion
of organisms intolerant of low dissolved oxygen and organically
enriched water, the stream is considered severely degraded.
However, even those animals which can tolerate such conditions
reguire some oxygen, and streams may become so heavily loaded
with oxygen depleting materials that no animals can exist. Toxic
materials can also remove a population of bottom-dwelling animals
although the habitat may be otherwise favorable.
A comparison of the biological community both upstream and
downstream from a waste source thus provides a valuable clue to
the condition of the bottom and the purity of the surrounding
waters. However, since the bottom animal population inhabiting
any particular area is dependent upon many factors, including the
characteristics of the substrate, stream flow, currents,
temperature, light and depth, comparisons are best made between
similar habitats.
Attached^Algae
Algae (non-vascular aquatic plants), like all green plants,
require nutrients for growth. In addition to many trace
elements, they take up measurable quantities of nitrogen and
phosphorus. All other factors being favorable, the higher the
concentration of these nutrients, the greater will be the density
of algal growth.
Attached algae can cover all suitable substrata on the stream
bottom and are a very important food source for many of the
bottom-dwelling animals. Since these algal forms are stationary,
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they reflect the quality of the water which has passed over them.
Certain forms, such as some of the blue-green algae, are typical
of organically enriched waters. Decreased water transparency can
be detrimental to attached algae populations by removing
necessary sunlight. This can occur in silt laden waters or by
the introduction of highly colored wastes.
Slime Growths
Biological slimes, commonly represented by the filamentous
bacterium Sfihaerotilus, can be a problem in streams subjected to
nutrient loading from a variety of waste materials. These
growths, non-esthetic in appearance, can blanket the stream bed
and render whole areas of a stream unsuitable for developing fish
while destroying the habitats necessary for desirable bottom
dwelling animals. Waste materials utilized by these slime
growths include carbohydrates, sugars and nitrogen. Often these
growths are more noticeable in winter since competition for the
nutrients with the more cold sensitive forms is reduced.
8
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SECTION IV
SELECTION OF STUDY SITES
Water and biological samples were collected from nine study
sites. Five sites involved log rafting, two included flow-
through log ponds, one included a flow-through log pond and a wet
deck, and the other had a closed log pond (no discharge) with a
wet deck ( a wet deck is an on-land stack of logs that is
generally kept wet in warm weather to prevent excessive drying
and consequent checking). The individual sites are discussed in
more detail in Section VI.
Several factors were considered in the selection of study sites.
These included possible interference from other waste sources;
excessive dilution by the receiving waters; suitable conditions
for biological studies; and permission of the companies involved.
Since one of the main project objectives was to determine the
effects of log handling and storage on water quality,
interference from other waste sources was to be at a minimum.
This criterion tended to eliminate many sites from further
consideration. Excessive dilution by the receiving waters was
considered undesirable for the study of flow-through log ponds
and the runoff from wet decks. Therefore, consideration was
limited to sites on small streams where there was more likely to
be a change in water quality.
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SECTION V
METHODS OF SAMPLE COLLECTION AND ANALYSIS
WATER CHEMISTRY
Collection and Preservation
All but two of the water samples for chemical analysis in our
studies were grab samples. The method of collection varied; for
all deep samples and some shallow samples either a Kemmerer
sampler or a Van Dorn sampler was used. The remaining shallow
samples were either collected in a bucket or by dipping the
sample container into the water. Samples from the log rafting
sites were collected near the stream bottom to better detect any
possible effect from settled bark. Unstabilized samples were
iced immediately and were in the laboratory within 24 hours after
collection. Samples for COD and organic carbon analysis were
preserved by adding 10 ml of concentrated sulfuric acid per liter
of sample. Mercuric chloride, 10 ml saturated solution per liter
of sample, was used to stabilize the samples for nitrogen and
phosphorus analysis. In the laboratory all samples were stored
at 5°C.
Field Analysis
Temperature, dissolved oxygen (DO), and some of the pH
measurements were performed in the field. DO concentrations were
determined by a DO meter or the Winkler-Azide titration method.
McHugh, et al (1964) reported that the Winkler method appeared to
give low results with log pond waters. A comparison was
therefore made using a calibrated DO meter and the Winkler-Azide
method to determine the DO concentrations in a sample of log pond
water having a COD of 87 mg/1. With a full-strength sample at
room temperature the Winkler-Azide method showed 7.9 mg/1 of DO
compared to 8.25 mg/1 for the DO meter, or a difference of 0.3
mg/1. The difference became less as the sample was diluted with
distilled water. At dilutions yielding COD concentrations of 32
mg/1 and less, the differences were 0.1 mg/1 or below, which was
not considered signficant at the COD concentrations encountered
in this study.
LlfeoratgrY_Analyses
In the laboratory the number of analyses performed on each sample
varied. The analyses for chemical oxygen demand (COD),
10
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biochemical oxygen demand (BOD), pH, conductance, suspended
solids (SS) , volatile suspended solids (VSS), color and chlorides
were performed according to Standard Methods (APHA 1965). The
methods used for determining total organic carbon (TOG),
orthophosphate, Kjeldahl nitrogen, nitrates, and turbidity are
given in FWPCA Methods for Chemical Analysis of Water and Wastes
(OSDI 1969). The procedure described by Felicetta and McCarthy
(1963) was used in determining Pearl Benson Index (PBI)
concentrations. In this report PBI concentrations are reported
in milligrams per liter (mg/1). One mg/1 of PBI equals 10 ppm of
10 percent apparent spent sulfite liquor. This test, commonly
used in the wood pulp industry, was used in this study to
indicate the same type of reactive ligneous matter.
BIOLOGY
Biological field and laboratory methods were generally those
prescribed by Standard Methods (APHA 1965) , Limnological Methods
(Welch 1948) and The Practice of Water Pollution Biology.
(Mackenthun 1969)7
l°.t£ om_Dwe 1 1 i ng_Or gani §JBg
Bottom fauna stations in the log rafting areas were usually
established at three points on a transect across the stream: Mid-
stream and the two quarter points. In some cases, samples were
collected only at certain points on either side. One Ponar grab
sample was collected at each station. This sampler, enclosing an
area of 538cm2 (0-58 ft2) was well suited to the silty-sand and
debris bottom types common in the rafting areas.
The streams were narrow and tended to have uniform bottom types
at each transect at the log pond and wet deck study sites.
Therefore, the three samples collected across the stream in these
areas were considered sub- samples of the same station. They were
designated as follows: A - right side facing downstream, B - mid-
stream, and C - left side facing downstream. Only the two side
samples were collected in very narrow streams. The Ekman grab
sampler was used at most of the stations on Elk Creek and was
more applicable to shallower, softer bottomed streams than the
Ponar sampler. The Ekman enclosed an area of 232.26 cm2 (0.25
ft2) . The Surber square-foot sampler was used at the remainder
of the study sites and was designed for shallow rock and gravel
bottoms .
11
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Non-quantitative bottom samples were collected where possible
with a dip net or by overturning rocks or other materials at the
shores. This supplemented data collected by the quantitative
devices. The dredgings or bottom materials collected by the
various sampling devices were washed through a U.S. Standard No.
30 sieve and were preserved in the field in a 10 percent formalin
solution.
In the laboratory, the dredging were rinsed in a U.S. Standard
No. 30 sieve,placed in trays, the bottom animals removed and
preserved in 70 percent alcohol. Rose Bengal or phloxine B stain
was frequently added to the samples before rinsing to facilitate
the sorting process. The organisms were identified to genera
when possible. Appropriate factors converted the counts per
sample to numbers per square meter of stream bottom.
The identity and numbers per square meter of the bottom animals
collected at each station are presented in the Appendix. The
numbers were rounded to the nearest whole. The number of
different genera determined for each bottom sample represents the
minimum number of genera present. Certain forms such as worms or
leeches were not identified beyond their broader classifications.
Other forms, such as immature mayflies or stoneflies, could not
be clearly identified beyond the family level. Unknown organisms
and pupae were included in the total number of organisms but not
tabulated as separate genera unless it was obvious they could not
be mistaken for other forms.
The volume of bark and detrital material retained on the sieve
from the log rafting area bottom samples was determined by
displacement. After the benthic organisms had been removed, the
material was drained on absorbent toweling for one minute and
then placed in a graduated cylinder containing a known volume of
water. The resulting displacement approximated the volume of
material and was reported in cubic centimeters per Ponar grab
sample.
Attached Algae and Slime Growths
Attached algae and slime growths were collected from rocks, logs
and pilings and preserved in 3 percent formalin. Identification
was conducted with a compound microscope at 450 to 1,000
magnifications. Samples of filamentous slime bacteria were
stained with cotton-blue lactophenol before examination.
12
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PHYSICAL OBSERVATIONS
Light penetration of the water was measured in a number of
locations with a 20 cm Secchi disc. Observations of the water
surface, stream bottom, water depth, shoreline, flow
characteristics and attached growths were routinely recorded.
Flow was measured at four of the study sites with either a Price
type or a pygmy current meter.
13
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SECTION VI
RESULTS
LOBSTER CREEK
Lobster Creek study site is located south of Alsea, Oregon.
Here, there is a sawmill and limited log storage facilities.
About 66,000-80,000 m3 of logs are handled annually. Douglas-fir
is the predominant species with some cedar and hemlock. These
logs are hauled in by truck, stacked in a dry deck (no
sprinkling), mechanically debarked, and placed in the log pond
for temporary storage. Generally there are no more than a few
days supply of logs in the pond.
The log pond is a flow-through type located on Meadow Creek, a
small tributary of Lobster Creek. The pond covers approximately
1.2 ha, has an average depth of about 2 m,and a maximum depth of
about 4.6 m. Normally only the downstream half is used for
holding logs. If the flow of Meadow Creek is not adequate to
maintain water levels in the log pond, additional water is added
by pumping from Lobster Creek. This was not necessary during
this study. It is approximately 0.3 km from the log pond
spillway to the confluence with Lobster Creek.
Meadow Creek has a drainage area of approximately 3.9 kmz. Most
of the area upstream from the log pond is forested while
downstream there is a cattle pasture along a portion of the
creek. Most of the Lobster Creek drainage is forested with
some cattle pastures and hay fields in the relatively level
valley areas. In the study area cattle had free access to
Lobster Creek, which is a spawning area for silver and chinook
salmon, steelhead, and cutthroat trout (OSWRB 1965) .
A reconnaissance was made in March and more detailed sampling
conducted in June and September 1969. There were two biological
sampling stations on Meadow Creek and four on Lobster Creek (Fig.
1). The stream bed of Meadow Creek was not uniform throughout
the study area. At station L-l upstream from the log pond the
bottom was composed of silty-sand and gravel as compared to
predominately bedrock and cobbles at station L-U near the mouth
of Meadow Creek. At all four sampling stations on Lobster Creek
the bottom material consisted mainly of rock, cobbles, and
gravel. Water depths were relatively shallow in both June and
September, not exceeding one-third meter (Table 1).
-------
Station
No.
L-l
L-2
L-3
L-4
L-5
L-6
L-7
L-8
Station Description
Meadow Creek about .6 km above log pond
outlet works.
Log pond just above outlet works.
Meadow Creek about 15 meters below log
pond outlet works.
Meadow Creek just above Lobster Creek.
Lobster Creek just above Meadow Creek.
West bank of Lobster Creek about 60 meters
below Meadow Creek.
East bank of Lobster Creek about 60 meters
below Meadow Creek.
Lobster Creek about 185 meters below Meadow
Creek. At downstream end of pool.
Note: Not to scale.
N
Meadow Creek
Figure 1. Lobster Creek study site
15
-------
Table 1. LOBSTER CREEK STUDY SITE BOTTOM DWELLING ORGANISMS
Station No.
Samples
June 11, 1969
L-l
L-4
L-5A
C
L-6
L-7
September 3, 1969
L-l*/
L-4
L-5A
C
L-6
L-7
L-&
2a_/
2a/
1
1
1
1
1
1 ^
1
1
1
1 .
1
No.
Genera
20
17
11
10
17
13
16
4,
9
11
14
11
16
No./m2
1 ,731
1,285
217
240
304
457
-
44
153
691
765
1,055
-
Depth
(cm)
15
15-30
15-30
15-30
15-30
15-30
15
6-15
15
15
15-30
15-30
15-30
Bottom Type
Silty-sand, gravel
Bedrock, cobbles
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Gravel
Bedrock, cobbles
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
~j/Pooled data.
b/ Non-quantitative sample only.
-------
Water quality was good upstream from the log pond in June and
September (Table 2). Dissolved oxygen was high (9.0-10.2 mg/1)
while COD (2-4 mg/1), suspended solids (1-2 mg/1), and turbidity
(1-2 mg/1) were low. There were 20 genera of organisms in the
quantitative sample collected in June and 16 genera in the non-
quantitative samples taken in September. The high percentage
(42X) of sludgeworms in the June samples was probably a
reflection of the silty-sand bottom. Neither this material nor
sludgeworms were evident in September. The predominant organisms
in September were caddisfly larvae, mayfly nymphs, and midge
larvae (App. A).
There was a sharp color contrast between the upper and lower ends
of the log pond. The upstream end was greenish, indicative of
algae and other aquatic plants; the downstream end where the logs
are kept was dark. Transparency at the spillway (L-2) as
measured with a Secchi disk, was 0.76 m in June and 0.23 m in
September. Dissolved oxygen at L-2 ranged from 6.3 mg/1 in March
to zero in September. COD in the summer averaged about 15 times
more at L-2 than upstream at L-l. FBI concentrations in June
were 8 times higher at the spillway than at L-l and were still 5
times higher downstream at the mouth of Meadow Creek. Increased
waste loading from the logs, decreased flow in Meadow Creek and
warmer summer temperatures all contributed to a lowering of water
quality at the spillway.
Abundant growths of Sghaerotilus covered mayfly nymphs and gill-
breathing snails near the mouth of the creek in March. Further
upstream, about 46 m downstream from the log pond, stonefly and
mayfly nymphs were similarly entangled. A coho salmon fry,
estimated to have hatched the previous October or November, was
captured at the same location. Water quality downstream from the
pond in March was apparently good enough to support organisms
commonly associated with clean water. However , the discharge
from the log pond obviously contained sufficient nutrients to
support the smothering growths of §p_haerotilus.
Only sparse amounts of SjDhaergtilus were seen at the mouth of
Meadow Creek in June, and none was observed in September. This
reduction was probably due to increased water temperature.
Abundant growths of the blue-green algae Qscillatoria, Phormidium
and Ly.ngby_a covered the stream bed at the mouth in September.
PhO£ffii^±liffi is associated with organically enriched waters, but
less frequently than Qscillatoria.
The water was still dark at the mouth of Meadow Creek (L-4). In
September the color intensity was 12 times that observed at L-l.
17
-------
Table 2. LOBSTER CREEK STUDY SITE WATER CHEMISTRY DATA
CO
Sta . Fl ow Temp .
No. (I/sec) (°C)
March 3, 1969
L-2 6.3
June 11, 1969
L-l 12.74 12
L-2 18
L-4 15.29 17
L-5 424.71 14
L-6
L-7
September 3, 1969
L-l 1.98 11
L-2
L-3 1.27 19
L-4 2.27 14
L-5 118.92 14
L-6
L-7
L-8 14
DO Cond.
.(rag/I) pH lfmhn
10.2 7.0 62
0.5 6.3 64
8.5 7.0 69
10.9 7.3 44
9.0 6.1 72
0 6.0
2.4 6.2 95
9.0 6.5 143
9.5 6.7 .52
9.6
Ortho
SS VSS Color Turb PBI COD BOD P TKN
.(rna/l) (ma/]) Pt. Co.. Jksn (mg/1) (mg/1) (mg/1) (mg/1) (mg/1)
17
22 2221
72 68 7 16 33 6
88 6 11 15 3
14 2 1131
1
4
1 1 10 1 3 4 <1 .024 0.1
55
56 28 200 18 2 35 2 .026 1.1
5 5 120 11 1 13 <1 .077 0.2
1 1 10 1 1 4 <1 -015 0.2
<1
1
<1
N03
. (mg/n
0.1
0.01
0.05
0.02
-------
Reaeration along the lower portion of Meadow Creek was good,
giving DO concentrations at the mouth of 8.5 mg/1 in June and 9.0
mg/1 in September. Although the DO levels were high the bottom-
dwelling animals were not indicative of clean water conditions.
Seventeen genera were found in June. Of the total population of
organisms 54 percent were fingernail clams, 29 percent midge
larvae, and 13 percent sludgeworms. Fingernail clams are
sometimes associated with degraded conditions and sludgeworms can
tolerate many types of organic pollution. There were no
caddisfly larvae or mayfly nymphs, and only one stonefly nymph
was collected (App. A). Poor conditions continued into
September. The increase in algal mats and lower streamflow at
this time could have adversely decreased the available habitats.
Only four genera of organisms were collected and were composed of
only one stonefly nymph, two midge larvae, one beetle larva, and
one blackfly larva (Table 1, App. A).
The flow from Meadow Creek tended to hug the east bank of Lobster
Creek for the first 60-90 m. This was evident because of the
darker color of Meadow Creek water. Stations L-6 and L-7 are
near the west and east banks, respectively, of Lobster Creek and
60 m downstream from Meadow Creek. Station L-7 was influenced by
Meadow Creek while L-6 was not. Downstream from L-6 and L-7 a
long pool extends nearly to Station L-8. The flow of the two
creeks apparently became mixed in this pool.
Water quality was generally good in Lobster Creek with the
exception of some slight differences near the east bank just
downstream from Meadow Creek. Dissolved oxygen was high (9.5-
10.9 mg/1) , the amount of oxidizable matter was low (COD < 1-U
mg/1), and the water was clear except where the flow of Meadow
Creek hugged the east bank. Moderate amounts of Sp.haerotilus
covered the rocks on the right bank of Lobster Creek downstream
from Meadow Creek in March. These growths were not present in
June or September, probably as a result of higher water
temperatures. There were slight differences between the bottom
animal populations at stations L-6 and L-7. At L-7 there was a
higher percentage of midge larvae in both June and September as
compared to L-6. In September there were sludgeworms at L-7 but
no mayfly nymphs, while at L-6 there were mayfly nymphs and no
sludgeworms. These differences may have been due to a degrading
effect by the flow of Meadow Creek. However, since the
differences are slight, they also may have been partly related to
natural variation in the distribution of the bottom dwelling
animals.
Meadow Creek's lack of impact upon the biology of Lobster Creek
was due largely to the relative sizes of the two streams. The
19
-------
flow in Lobster Creek was 27 times that of Meadow Creek in June
and over 52 times the flow in September (Table 2).
In summary, dissolved oxygen almost became depleted in the
downstream end of the log pond during warm weather. There was
sufficient carbon and other nutrients in the discharge from the
pond to support abundant growths of Sghaergtilus in Meadow Creek
when temperatures were low enough. The log pond water was
esthetically objectionable in color and adversely affected the
bottom organisms in Meadow Creek during the summer. There were
only slight, localized effects on water guality in Lobster Creek
because of dilution.
ELK CREEK
Elk Creek study site is west of Noti, Oregon, in the Long Tom
River drainage, a sub-basin of the Willamette River. The log
storage facilities consist of a flow-through log pond on Elk
Creek. Logs brought in by truck are stored in the pond until
needed, then hauled away. Storage varies from almost nothing to
3,500-4,700 m3 of logs. An average of 5,900 m3, predominantly
Douglas-fir, pass through the pond annually.
The pond has a surface area of about 10 ha. The maximum depth in
the stream channel is about 4.6 m; the upper end of the pond is
shallow. Accumulated bark and dirt are removed periodically by
dredging.
Average annual precipitation in the area is about 127-152 cm.
Much of the Elk Creek drainage is forested, especially in the
hilly areas. Upstream from the study area Elk Creek flows
through open valleys used for cattle pasture and hay fields.
There are also pastures and farm land about 1.3 km downstream
from the pond. Cattle had free access to the creek near the
sampling station located upstream from the log pond.
Biological and water chemistry samples were collected in October,
1968, and July, 1969 (Tables 3 and 4). One sampling station was
established upstream from the pond and four downstream (Fig. 2).
The stream bed was not uniform throughout the study site.
Upstream from the pond at E-l the bottom was sandy silt. Water
depth was 0.61 m in October, 1968, but dropped to 0.15 m and less
the next summer. Immediately downstream from the spillway the
stream bed was rocky and contained several riffles at E-3.
Within 0.2 km further downstream the stream gradient flattened
20
-------
Table 3. ELK CREEK STUDY SITE BOTTOM DWELLING ORGANISMS
Station
October 10, 1968
E-lb/
E-3
E-4
E-5^/
July 23, 1969
E-l
E-3^/
E-4
E-5
No.
Samples
1
1
4
1
3
1
3
3
No. / No./m2-7
Genera-
6
9 1,895
7 733
13
6 409
9
13 2,008
17 1,434
Depth
cm
61
15-30
30-61
30-61
30
30
61-76
30-61
Bottom
Sandy-silt
Type
Rock, cobbles, gravel
Sandy-silt,
Sand, bark
Sandy-silt
Rock, cobbl
Sandy-silt,
Sandy-silt,
bark, branches
es
gravel , branches
bark, wood
a/ Pooled data.
F/ Non-quantitative sample only.
-------
Table 4. ELK CREEK STUDY SITE WATER CHEMISTRY DATA
ro
ro
Sta.
No.
October
E-l
E-2
E-3
July 23
E-l
E-2
E-3
E-4
E-5
Fl ow Temp .
(I/sec) °C
18, 1968
11
11
12
, 1969
45.3 16
18
21
22
84.9 20
DO Cohd. SS VSS Color Turb.
,(mg/l) pH ymho Y(mg/l) ((mg/1) Pt. Co. Jksn
8.7
10. &/
10.2
8.5 7.1 43 16 2 50 14
0.4 6.2 47 4 3 50 3
6.7
6.4 6.8
6.9 7.2 49 6 2 50 3
PBI COD TOC BOD
(mg/1 ) (mg/1,) (mg/l> f mg/1.^
0.5 10
2.4 14
14
13
2.5 14
4
7
5
4 3
5
5
4 2
Ortho-P TKN NO~-N
(mg/1,* fing/lnmy/1
— V — "^" ' / ' " "\ -"•••• - /A - 'i
.013 0.4 0.3
.009 0.6 0.39
.009 0.4 0.48
b/ Average of 11.0 mg/1 at 15 cm and 10.2 mg/1 at 1.37 M depth.
-------
Station
No.
E-l
E-2
E-3
E-4
E-5
Station Description
Elk Creek about 2 km (via highway)
upstream from log pond spillway.
Log pond at spillway.
Elk Creek at riffles about 30 meters
downstream of spillway.
Elk Creek at first bridge downstream
(about .25 km) of log pond spillway.
Elk Creek at second bridge downstream
(about 1.3 km of log pond spillway.
I
N
Log Pond
Figure 2. Elk Creek study site
Elk Creek
23
-------
out and the stream was somewhat slower flowing with shallow
pools. The stream bed was sandy-silt at E-4, changing to silty
sand and sand at E-5. Water depth ranged from 0.3 to 0.76 m at
these two stations and varied little between seasons. Bark
chunks, sunken logs, and branches were common at the lower two
stations.
At station E-l the water was clear while at the pond and
downstream it was dark, a characteristic of log pond waters.
Transparency (Secchi disk) just upstream from the spillway was
limited to about 0.61 m at both seasons. The water was dark,
foamy and displeasing in appearance as it cascaded over the rocks
below the spillway. Somewhat contradictorily, samples collected
from E-l, E-3, and E-5 in July had the same color intensity, 50
color units, as measured by the Platinum-Cobalt method. This
apparent discrepancy can be partially explained. The Platinum-
Cobalt method does not actually measure the color of a sample,
but compares the transmission of light through the sample and
through standard solutions of chloroplatinate. This method is
not reliable with certain colors and possibly not with certain
log pond waters. In July the water at E-l was shallower than at
stations E-2, E-4, and E-5. This could result in the water
appearing to have less color than at the other stations.
Although the dissolved oxygen was nearly depleted (0.4 mg/1) just
upstream from the spillway in July, reaeration of the water
cascading over the spillway raised oxygen levels to over 6 mg/1.
There was a slight increase in COD concentrations from upstream
to downstream, from 10 to 14 mg/1. PBI concentrations in July
were about five times higher downstream from the pond than they
were upstream. The other chemical parameters studied varied
little between up and downstream from the pond (Table 4).
Thick mats of an unidentified filamentous green algae covered the
face of the spillway. Small amounts of Batrachosgermum, a
filamentous green alga common to colder water, were collected at
E-l and E-3 in July. The stream bed at E-l was a favorable
habitat to the sediment-associated midge and fly larvae and
sludgeworms which predominated. A non-quantitative sample in
October contained mostly horsefly and cranefly larvae and
sludgeworms. The following July, midge larvae comprised 6 to 11
percent and sludgeworms from 8 to 20 percent of the bottom
dwelling organisms collected in three sub-samples (App. B).
Normally, a habitat such as the riffle at E-3 would support
diverse numbers of organisms. However, a sample from this
location in October contained 84 percent sludgeworms and only 6
24
-------
percent mayfly nymphs. The following July, a non-quantitative
sample at the same location contained about half midge larvae and
half mayfly nymphs (App. B) .
A similar situation was seen at E-4. Sludgeworms comprised over
80 percent and midge larvae over 10 percent of the bottom-
dwelling organisms in October. The next July, mayfly nymphs made
up 40 percent of the organisms and sludgeworms only 35 percent
(App. B). The lack of variety at these two stations in October
follwed by increased diversity in July may have been due as well
to a decrease in organic sediment as with seasonal fluctuations
in the mayfly populations.
The best water quality, as reflected by clean water-associated
organisms, was exhibited at E-5. Two genera of stonefly nymphs
and five genera of mayfly nymphs were evident in non-quantitative
sampling in October. Quantitative sampling the following July
revealed the bottom organisms to be made up of 42 percent mayfly
nymphs and 28 percent midge larvae. Sludgeworms composed an
insignifcant part of the population at both seasons. Seven
different genera were collected in non-quantitative samples in
addition to seventeen genera collected in the grab samples in
July (App. B) .
The frequently encountered bark chunks and logging debris
downstream from the pond could be damaging to the stream if
present in sufficient amounts. The increase in desirable bottom-
dwelling organisms downstream from the pond, however, can partly
be attributed to increased numbers of habitats being made
available in the bark and tree debris. Biologically, the log
pond did not appear to have a very degrading effect upon the
stream. Esthetically, there was definite degradation.
ROW RIVER
Row River study site is at Culp Creek, Oregon, and includes a
sawmill and plywood plant near a portion of the Row River and
Culp Creek. Logs are trucked to the site and those not used
immediately are stored in wet decks.
Some logs are then taken to the pond, removed for debarking, and
replaced temporarily. Some unbarked logs are also stored there.
About 118,000-142,000 m3 of logs are handled annually,
predominantly Douglas-fir with some cedar and hemlock.
25
-------
The log pond is a flow-through type on Gulp Creek (Fig. 3). The
dam at the downstream end of the pond is about 46 m upstream from
the confluence with the Row River. Surface area of the pond is
about 2.5 ha. The wet decking area is located adjacent to a bend
in the Row River. Water for sprinking the cold decks in the
summer is obtained by pumping from the river near station R-3.
There were about 7,000 m3 of logs in the wet decks in August,
1969. A drainage ditch runs along the southern edge of the wet
decking area and receives seepage from nearby springs, glue
wastes from the plywood plant, and part of the runoff from the
wet decks. The wastes from the plywood plant did not appear to
interfere with the study.
Most of the drainage area upstream from the study site is
forested. Average annual precipitation in the area is about 127-
152 cm (OSWRB 1961). At the U.S. Geological gauging station
about 5 km downstream from Gulp Creek the mean annual yield of
the/Row River over a 33 year period was about 526.76 x 10* m3.
The minimum recorded flow at this point was 0.28 m3 per second.
Two biological stations on Gulp Creek and five on the Row River
were sampled in June and August, 1969 (Figure 3). At R-l,
upstream from the log pond, the bed of Gulp Creek was composed of
cobbles, gravel, and sand. Downstream, bedrock predominated from
the dam to the confluence with the Row River. The creek was
shallow; water depth was 15 cm at R-l and 3-15 cm at R-2. The
stream bed of the Row River at R-3, upstream from Gulp Creek, was
composed of bedrock, rock and a few cobbles. The bottom
materials were smaller in size at the downstream locations and
were predominated by cobbles and gravel. The downstream sites
tended to be more pool-like while the upstream location was
characterized by swifter and more turbulent flows. Depths at the
upper stations ranged from 15-60 cm, while the downstream
stations were 30-60 cm deep.
The water was dark and foamy as it discharged from the log pond
at R-2. Transparency in the pond, as measured with a Secchi
disc, was 0.53 m in June and 0.61 m in August. In contrast, the
water was clear at the upstream station. Color was substantially
higher downstream from the pond, a four-fold increase in June and
a 16-fold increase in August. COD was six to seven times higher
(4-30 mg/1) at R-2 as compared with R-l. While the FBI was seven
times higher at the downstream location in June, the two stations
had about the same values in August. Dissolved oxygen, although
very low in the pond at the dam (1.1 mg/1) increased
substantially (7-8.5 mg/1) through reaeration over the spillway
(Table 5).
26
-------
Station
No.
R-l
R-2
R-3
R-4
R~5
R-6
R-7
R-8
Stations not shown
R-9
R-10
Station Description
Gulp Creek about .56 km above log pond.
Gulp Creek above confluence with Row River.
Row River about .24 km above Gulp Creek.
Row River about .64 km below Gulp Creek.
Runoff from north side of cold decking area.
Flows into Row River.
Row River above drainage ditch. About 1.4 km
below Gulp Creek.
Drainage ditch above confluence with Row River.
Row River about 1.2 km below drainage ditch.
Water applied to last bay at west end of cold
decking area. Sample collected from leak
in pipe.
Composite sample of drippings from logs in
1st bay at western end of cold decking area.
Drainage
Ditch
Cold
Decking
Area
ROW RIVER
Figure 3. Row River study site
ROW RIVER
27
-------
Table 5. ROW RIVER STUDY SITE WATER CHEMISTRY DATA
IVJ
cx>
Sta. Flow Temp.
No. fl/sec) °C
June 18, 1969
R-l 39.6 14
R-2 22
R-3 3454.3 20
R-4 21
R-7
August 28, 1969
R-l 5.7 13
R-2 22
R-3 707.9 18
R-4 19
R-5
R-6
R-7
R-8
R-9
R-10
DO
(mg/1 )
9.8
8.5
8.9
8.7
10.0
7.4
9.6
9.4
9.7
PH
7.6
7.6
7.1
7.9
6.6
6.3
6.3
6.5
7.1
6.9
Cond. SS
ymho (mg/1 )
6
7
2
2
80 4
88 11
80 1
80 2
125 8
170 108
87 1
50 4
VSS
(mq/1 )
5
5
2
2
2
11
1
1
<1
30
1
4
Color
Pt. Co.
10
40
5
5
5
80
5
5
80
200
5
80
Turb.
Jksn
7
10
3
3
2
4
<1
1
7
27
1
2
PBI
(mg/1
2
15
1
1
2
3
< 1
<1
2
103
<1
5
Ortho
COD BOD P TKN NO -N
) (mg/1) (mg/1) (mg/1.) (mg/1) (mg/1.)
4 1
25 3
4 1
6 1
151
4 .009 0.1 .02
30 4 .01 0.5 <.01
4 .007 0.3 .02
5
43 3 .011 0.6 <.01
6
153 14 .049 1.4 .03
7
4
40 5 .056 0.4 <.01
-------
a filamentous blue-green alga common in shallow water,
was sparse at R-l in June. At the same time at R-2, abundant
mats of the blue-green alga Anabaena covered the rock downstream
from the dam. This alga is frequently associated with
organically enriched waters.
Large amounts of Mougeotia, a common green filamentous alga, were
growing at R-l in August. The stream bed downstream from the dam
at this time was abundantly covered with deteriorating mats of
this alga. Oscillatoria, a filamentous blue-green alga
frequently in organically enriched waters, was present in large
amounts in these mats. No Sp.haerotil.us was collected from Gulp
Creek.
There was a dramatic reduction in the number of genera of bottom-
dwelling animals at R-2 as compared with R-l at both seasons. In
June, the genera decreased from 15 to 3, while in August, the
number decreased from 26 to 1 (Table 6).
The upstream station, R-l, was characterized by organisms
commonly associated with good water quality conditions. In
June, the bottom- dwelling animals were comprised of 43 percent
caddisfly larvae, 17 percent mayfly nymphs, and 15 percent
stonefly nymphs. In August, continued good conditions were
indicated by 43 percent stonefly nymphs, 22 percent mayfly
nymphs, and 6 percent caddisfly larvae (App. C).
Downstream from the pond at R-2 in June only a few cranefly
larvae, mayfly nymphs, and gill-breathing snails were present.
In August, only the gill-breathing snails remained (App. C).
There can be no doubt that the log pond had a degrading effect
upon the bottom dwelling animals of Gulp Creek. Even though a
different bottom type downstream from the pond reduced the number
of habitats available for desirable organisms, a greater variety
of animals would have been expected than was found. Higher
temperatures at R-2 as compared to downstream (22.5°C and 13°C)
were also a probable cause of the decreased diversity.
Esthetically, the creek was degraded and presented an unpleasant
scene downstream from the log pond.
The runoff from the wet decks in August was similar in quality to
the log pond waters. A composite sample (R-10) of drippings from
logs in one of the wet decks had a BOD of 5 mg/1 and a COD of 40
mg/1. Part of the sprinkling runoff flowed in small rivulets
29
-------
Table 6. ROW RIVER STUDY SITE BOTTOM DWELLING ORGANISMS
co
o
Station
June 18, 1969
R-l
R-2
R-3
R-4
R-6
August 28, 1969
R-l
R-2
R-3
R-4
R-6
R-8
No.
Samples
2
i ^/
b/
3
1
2
&
2
3
3
3
No. ,
Genera-'
15
3
8
9
8
26
1
20
13
13
13
No./n>
480
-
-
83
325
1,138
-
755
288
826
1,015
Depth
cm
15
3-15
15-60
30-60
30-60
6-15
3-15
15-30
30-60
30
30
Bottom Type
Cobbles, gravel
Bedrock
Bedrock, rock,
Cobbles, gravel
Rock, gravel
Cobbles, gravel
Bedrock
Bedrock, rock,
Cobbles, gravel
Cobbles, gravel
Cobbles, gravel
, sand
cobbles
cobbles
a/ Pooled data
5/ Non-quantitative sample only
-------
down the bank into the river. A sample from one of these
rivulets (R-5) had a BOD of 3 mg/lr COD of 43 mg/1, and a color
intensity of 80 color units. A large portion of the surface
runoff appeared to flow into the drainage ditch along the
southern edge of the wet decking area. Since this ditch also
received glue wastes from the plywood plant, the data from
station R-7 cannot be used in characterizing the quality of wet
deck runoff. The amount of water applied to the wet decks was
not measured and it was not feasible to measure the surface
runoff. Seepage along the river bank adjacent to the wet decking
area indicated that some water was seeping into the ground and
flowing laterally toward the river.
The water in the Row River was generally clear at all locations.
The flow from Gulp Creek, while dark and displeasing, soon
dissipated in midstream.
Gulp Creek had little measurable influence upon the chemistry of
the Row River. There was almost no difference in the levels of
chemical constituents up and downstream from the confluence of
the two streams. Dissolved oxygen remained high (8.7-9.8 mg/1)
throughout the river (Table 5) .
No Sjoaerotilus was collected from the Row River. Moderate
amounts of StigeocIonium, a green filamentous alga, and
P&2O?i
-------
Non.-quarvtitat.ive sampling at R-3 in June revealed three genera
each of caddisfly larvae and mayfly nymphs. In August,
quantitative sampling showed the bottom-dwelling animals to be
comprised of 34 percent mayfly nymphs and 20 percent caddisfly
larvae. Twenty different genera were collected in August (App.
C, Table 6). Good quality conditions prevaled during both
seasons.
Degraded biological conditions were not evident in the Row River
at the confluence with Gulp Creek. In June, a variety of
caddisfly larvae and mayfly and stonefly nymphs were collected in
the Row in areas strongly subjected to Gulp Creek water. The
same conditions were evident in August.
In June, caddisfly larvae comprised 62 percent of the bottom-
dwelling animals at R-4. Six different genera were collected
through non-quantitative sampling in addition to nine different
genera in the quantitative samples. In August, 13 genera were
collected in the quantative samples but 57 percent of the
organisms were gill-breathing snails generally associated with
clean water conditions. Mayfly nymphs comprised only 10 percent
of the organisms and riffle beetles made up 14 percent (Table 6,
App. C). Station R-6 had over 76 percent mayfly nymphs in June
and over 80 percent gill-breathing snails in August. The number
of genera increased from 8 in June to 13 in August (Table 6, App.
C).
The bottom-dwelling animal populations downstream from Culp Creek
were not well balanced in variety as at the upstream station. In
June, the downstream stations were characterized by high
proportions of caddisfly larvae or mayfly nymphs. In general,
the stream bed downstream seemed to have less attached algae and
diatoms which could be used for a food supply. The smaller
bottom materials could also have reduced the number of available
habitats needed for a greater variety of organisms.
The shading caused by increased stream cover at the downstream
sites may have decreased the amount of available sunlight needed
for attached algae and diatom production and hence resulted in
less food and subsequently less variety of organisms. It has
been shown, however, that this type of gill-breathing snail and
not reduced light can almost totally eliminate the attached
growths in woodland streams west of the Cascades (Phinney 1969).
This may have been the case in the Row River. The caddisfly
larvae and mayfly nymphs may have not been as successful as the
snails in competing for the available food supply in the
downstream reaches of the study site.
32
-------
Although there were profound changes in the bottom-dwelling fauna
up and down stream from the confluence with Culp Creek, it is
doubtful if they can be attributed to log handling and storage
practices. The flow in the Row River was 87 times that of Culp
Creek in June and 125 times the flow in September (Table 5).
This certainly was a major factor in the lack of impact of the
smaller stream upon the larger. There was no detectable effect
from the wet deck and the plywood glue waste discharge. Changes
in stream morphology coupled with natural changes in the bottom
populations are a more likely explanation of the differences
between the control station and the downstream stations. The
most serious problem in the Row River is probably one of
esthetics.
MIDDLE FORK OF THE JOHN DAY RIVER STUDY SITE
This site is at Bates, Oregon, and includes a portion of the
Middle Fork of the John Day River and the mouth of Clear Creek, a
tributary stream. Logs are hauled in by truck to a sawmill and
those not used immediately are stored in wet decks. A closed
pond adjacent to the sawmill contains logs taken from the wet
decks in addition to some held in reserve. Approximately 50
percent of the logs used are pine, the remainder being white fir,
Douglas-fir, and larch.
The log pond is located on the south bank immediately adjacent to
the river. Although there is no direct discharge from the pond,
some seepage undoubtedly reaches the river. When necessary, the
water is pumped from the river to maintain the pond level. The
two wet decking areas are located along the north bank of the
river, one upstream and the other downstream from the pond.
Water for these decks is pumped from the river just upstream from
the pond. Only the upstream deck, which was not being sprinkled
was in existance in May, 1969. The two decks were present in
August however, both being sprinkled. The upstream wet deck was
about 180 m long, contained about 4,700 m3 of logs (about 85
percent pine) and was being sprinkled its entire length. About
120 m of this deck was within 5-10 m of the river's edge. The
water became impounded at the base of the wet deck before flowing
down the bank in small rivulets. The downstream wet deck, about
90 m long, contained about 85 percent pine and was under
construction. This wet deck was located at the edge of the river
bank and about 75 percent of its length was being sprinkled.
\lthough the bank was moist, there were no signs of direct
•unoff. The amount of water applied to the wet decks was not
easured as it was not feasible to measure the runoff.
33
-------
Cattle had free access to the river in pastures both up and
downstream from Bates (estimated 1969 population of 300).
Domestic wastewater from the homes and sanitary wastewater from
the sawmill were treated in septic tanks. Apparent drainage from
these systems entered the river at a culvert opposite the
upstream wet deck and another culvert just upstream from the
lower wet deck. Children also mentioned septic tank seepage
along the south bank just downstream from Clear Creek.
Bates is approximately 15 km downstream from the headwaters of
the Middle Fork of the John Day River. The river elevation at
the town is about 1,220 meters. Most of the drainage area
upstream from the study site is forested. Average annual
precipitation is between 50 and 76 cm. Downstream from Bates
approximately 39 km of the river are used as spring Chinook
spawning grounds. Numerous tributary streams, including Clear.
Creek, are used by spawning steelhead trout (OSWRB 1962).
In August four samples were collected to determine the
pollutional characteristics of the wet deck runoff (Table 7).
These consisted of water applied to the wet deck (J-15), a
composite of log drippings (J-16), and runoff (J-3 and J-5). The
two runoff samples averaged 30 mg/1 of BOD, 99 mg/1 of COD, and a
color intensity of 170 color units (Table 8). These are
significant increases over the concentrations in the water
applied to the logs. The runoff samples had higher COD and color
concentrations than did the drippings from the logs. This
difference is attributed to contact with bark debris in the
ponded water at the base of the wet deck. The BOD to COD ratio,
0.3, indicates that there is a higher percentage of readily
biodegradable organic material than is found in many log pond
waters. The BOD, COD, and color concentrations in the runoff
here were higher than in the runoff from the wet decks at the Row
River study site probably because the logs at Bates had been
sprinkled for only two weeks and they were predominately pine
compared to mainly fir at the Row River site.
Four of the stations, J-2, J-9, J-10, and J-13, were sampled for
biological samples in May, 1969, before wet decking had started.
These, in addition to J-l and J-14, were also sampled in August,
1969, after approximately two weeks of sprinkling. A station
established in Clear Creek near its mouth was sampled during both
seasons (Fig. 4, Table 7) .
The bottom materials were generally similar throughout the study
site (Table 9). Rock, cobbles, and gravel predominated at the
four biological stations downstream from Clear Creek. Somewhat
34
-------
Table 7. SAMPLING STATIONS MIDDLE FORK JOHN DAY RIVER STUDY SITE
Station
No.
J-l
J-2
J-3
J-4
J-5
J-6
KoacR
(km)
0.0
.97
1.03
1.05
1.16
1.21
Station Description
MFJDR- at bridge above upper pasture.
MFJDR just above 1st cold deck.
Runoff from sprinkling of 1st cold deck.
At upper end of cold deck.
Clear Creek at confluence with MFJDR
Runoff from lower end of 1st cold deck.
Culvert discharging to MFJDR. Located on
J-7
J-8
J-9
J-10
1.22
1.24
1.34
1.72
J-12
J-13
J-14
1.93
2.9
5.79
Stations not shown
J-15
J-16
south bank across from downstream end of 1st
cold deck.
South bank MFJDR just above 1st bridge below
1st cold deck.
North bank MFJDR list below 1st bridge below
1st cold deck.
MFJDR at pump house.
Culvert discharging to MFJDR. Located on
south bank just upstream from 2nd cold deck
and downstream from J-10.
MFJDR just downstream from 2nd cold deck.
MFJDR about .97 km below 2nd cold de'ck.
MFJDR about 3.86 km below 2nd cold deck.
Water applied to 1st cold deck. Sample
collected from 1st sprinkler.
Composite sample of drippings collected from
logs in 1st cold deck.
a/ Gives approximate distance in kilometers below furtherest upstream station
Taken from road paralleling the river. Meant to show relative position
of stations.
b/ Middle Fork John Day River.
35
-------
Table 8. MIDDLE FORK JOHN DAY RIVER STUDY SITE WATER CHEMISTRY DATA
Sta. Flow Temp. DO
No. (I/sen °C (mq/1 )
May 26-27, 1969
J-2- 8.9
J-8 1698.8 14 3.8
J-10
August 18-19, 1969 Temp & DO
J-l
J-2 113.3 21 7.1
J-3
J-4 90.6 21 7.6
J-5
J-6
J-7
J-8 198.2 6.6
J-9
J-10 - 22 7.6
J-ll
J-12
J-13 22 7.0
J-14
J-15
J-16
pH Cond.
ytnho
91
69
readings taken
6.7 148
6.6 146
6.9 99
6.7 138
134
6.9 129
6.7 126
7.1 133
7.3 119
7.1 126
SS VSS
(mg/1.) (mg/1)
11 3
14 3
on August. 18.
1.8 1.6
1 <1
3.6 2
14 12
2.4 2
2.4 2
3.2 2
2 2
5.4 0.9
12 12
Color
Pt. Co.
40
20
Samples
35
200
10
140
40
35
40
45
35
70
Turb. PBI
Jksn (mg/1
12 <1
10 <1
collected on
1 <1
3 12
2 1
3 20
2 <1
1 <1
2 2
1 1
3 <1
3 12
Ortho
COD BOD P
) (mg/1 ) (mg/1 ) (mg/1)
12
12
12
August 19.
9
14 2 .06
84 22
4 1 .05
113 37
27 .1
8
12 1
10
9 1 .08
55
15 .1
14 2 .11
13 1 .08
10 1 .07
65 27 .18
TKN N03-N
(mg/1.) (mg/1.
0.4 .001
0.2 .01
0.4 .003
0.8 <.001
0.4 <.001
0.5 .004
0.8 <.001
-------
Table 9. MIDDLE FORK OF THE JOHN DAY STUDY SITE BOTTOM DWELLING ORGANISMS
Ul
-J
Station
May 26, 1969
J-2
J-4^-/
J-9
J-10
J-13
August 18, 1969
J-l
J-2
J-4^
J-9
J-10
J-13
J-14
No.
Samples
2
2
1
3
2
2
2
2
2
2
2
2
N°'a/
Genera-'
^ 24
12
15
16
23
23
22
39
21
28
30
31
No./m2 -f
1,852
403
638
757
1,323
3,663
1,718
4,112
622
1,227
3,753
4,686
Depth
cm
15-30
30-60
30
30-60
30-60
15
15
15
30
15
15
15
Bottom Type
Cobbles, gravel
Cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Gravel, silty-sand
Cobbles, gravel
Gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
Rock, cobbles, gravel
-' Pooled data.
-f Clear Creek.
-------
NOTE: Not to scale.
Some tributary streams below
2nd cold deck are not shown.
co
CO
North Bank
Log Pond
N
Middle Fork John Day River
2nd Cold
Deck
Figure 4. Middle Fork John Day River site
-------
smaller materials were found upstream from this point with
cobbles and gravel at J-2 and gravel and silty-sand at J-l.
Cobbles and gravel were common at the Clear Creek station.
The river was shallow; in May, most locations were 30 to 60 cm
deep, while in August most were 15 cm. The water was clear and
the bottom visible at all stations on the two streams in both
spring and summer.
There were other waste sources in addition to runoff from the
upstream and downstream wet decks. Cattle were pastured between
the following stations: J-l and J-2, J-12 and J-13, and J-13 and
J-14. They had access to the river in these areas and used it as
their water supply. Septic tank seepage may have begun reaching
the river just downstream from Clear Creek in addition to septic
tank drainage from culverts at J-6 and J-ll (Fig. 4).
Dissolved oxygen in August was sufficiently high to support
aquatic life throughout the study area (6.6-7.6 mg/1). Nitrogen
and phosphorus levels were low; there were little differences
upstream from the upper wet deck and the farthest two stations
downstream (NO3-N from 0.001 to <0.001 mg/1, ortho-P from 0.06 to
.0.08-0.11 mg/1, and TKN from 0.4 to 0.4-0.8 mg/1). Chemical
oxygen demand increased from 9 mg/1 at station J-l to 14 mg/1 at
J-2, possibly influenced by the cattle pasture between these two
stations. The COD was lower at J-9 and J-10 (9-12 mg/1),
possibly diluted by Clear Creek. The values at J-13 and J-14
were higher and comparable to those at J-2, perhaps influenced by
the downstream wet deck, the culvert at J-ll, and the two
downstream cattle pastures. Clear Creek was characterized by
generally lower levels of chemical constitutents than the Middle
Fork of the John Day River (Table 8).
No S|>haerotilus growths were observed in the Middle Fork of the
John Day River in May. E§SQU2£ulus, a submerged rooted aquatic
plant, grew in small amounts at the majority of stations.
Attached algae on the stream bottom increased from up to
downstream, possibly as a result of additions of nutrients. No
growths were observed at J-2, while there were moderate amounts
of the green algae Tetrasgora and Palmgdicty_on at J-9 and J-10.
The green algae Cladophora and Stigeoclonium grew in abundance at
J-13 along with lesser amounts of two common blue-green forms,
Nostoc and Plectonema. Large amounts of the latter two types of
green algae are often associated with enriched waters.
39
-------
was abundant at J-l in August and decreased
downstream until there was none at J-14. Attached algae was much
more abundant, both in variety and amount, in August than in May.
The amount increased from J-l to J-13 and then decreased at J-14.
The green algae Chaetoghora and attached diatoms sparsely covered
the rocks at J-l and J-2 in August. At J-9, probably in response
to wet deck runoff and septic tank wastes, moderate amounts of
Sp_haerotilus and abundant growths of the blue-green algae
£h2Emi.c|ium and Anabaena covered the rocks. These blue- green
forms are often associated with organically enriched waters.
Farther downstream at J-10 Sghaerotilus increased and blue-green
algae, mostly Phormidium and Qscillatoria, were abundant.
SgirogY£§.» a. green alga, became more apparent at this station.
Large amounts of Sp_haerotilus were growing directly downstream
from the culvert at J-ll. Station J-12, downstream from both
this point and the downstream wet deck, was characterized by
abundant Sghaerotilus intertwined with the green algae Sgirogyra
and Mgugeotia. The Sghaerotilus growths then decreased at J-13
and were not observed at J-14. The attached algae at this
station, the farthest downstream, was made up largely of moderate
amounts of diatoms and
The increased growth of attached algae and Sghaerotilus in the
downstream reaches of the study area was no doubt a response to
added nutrients or wastes. Although the chemical constituents
varied little from upstream to downstream, they represent only
the levels at the particular time the samples were collected.
The attached algae however, reflect what has passed over them for
an extended period of time. In addition, from the data available
it would be impossible to attribute changes in the attached
growths solely to wet deck runoff, septic tank drainage or cattle
wastes.
Good water quality conditions, as indicated by the bottom
dwelling animals prevailed in Clear Creek at station J-4 (Table
9, App. D). In May, the bottom population contained 50 percent
mayfly nymphs, over 28 percent caddisfly larvae and only 10
percent sludgeworms. A 9-fold increase in the numbers of
organisms from May to August, and an increase in the number of
different genera from 12 to 39 between these two seasons,
indicated both increased productivity and variety. The bottom
animals at the later season were made up of 29 percent mayfly
nymphs, 24 midge larvae, 5 percent stonefly nymphs, and 26
percent sludgeworms.
40
-------
Fifteen to 24 different genera were collected quantitatively at
each of the four stations sampled on the Middle Fork of the John
Day River in May (Table 9, App. D) . Non-quantitative samples at
the same locations contained from 5 to 10 additionally different
genera, indicating more variety. Although the bottom-dwelling
animals indicated generally good water quality in May there
appeared to be localized responses to possible waste sources.
Sludgeworms predominated at J-2, compromising 43 percent of the
population. The remainder of the population contained 34 percent
mayfly nymphs, 14 percent midge larvae and 1 percent caddisfly
larvae. The rather high percentage of sludgeworms may have been
a response to the cattle pasture just upstream.
Mayfly nymphs increased to 50 percent of the population and
caddisfly larvae to 16 percent while sludgeworms decreased to 13
percent at the next station downstream, J-9. These improved
conditions may have been partly a response to slightly different
physical conditions. The bottom was rockier than upstream and
because of the higher water at this season, the current was
swifter and the water more turbulent than at the other stations.
Since conditions here were slightly atypical of the rest of the
stream at this time, only one sample was collected.
Generally good water quality, as indicated by the bottom-dwelling
organisms, characterized the river in August (Table 9, App. D).
Productivity and variety had increased from May to August, shown
by an average increase per station of six genera and 1,400
organisms /m2. The number of different genera increased as the
stream progressed downstream. Twenty-one to 23 genera were
collected at stations J-l, J-2, and J-9 while from 28 to 31
genera were collected at stations J-10, J-13, and J-14. The
number of additional genera collected in non-quantitative
sampling at each of these locations ranged from four to 11. The
populations of bottom-dwelling organisms very likely increased in
August since the attached algal growths at that time represented
an abundantly available food source.
Riffle beetles were the predominant organisms at the first three
biological sampling stations. These organisms may be scarce in
streams with low dissolved oxygen and high sediment load. They
comprised from 27 to 37 percent of the bottom organsisms at J-l,
J-2, and J-9. Mayfly nymphs predominated at the last three
stations, comprising 38 to 40 percent of the populations at J-10,
J-13, and J-14.
4]
-------
Station J-l was sampled in August in order to detect any possible
effects from the cattle pasture upstream from J-2. There was
little difference in quality between these two stations. Mayfly
nymphs decreased from 27 percent at J-2 to 10 percent at J-9
while midge larvae increased from 5 to 31 percent between these
two stations. This may have been a localized response to a
combination of the upstream wet deck, the culvert at J-6, and the
flow from Clear Creek.
A two week period of wet decking in August did not appear to have
a deleterious effect upon the bottom-dwelling animals of this
section of the Middle Fork of the John Day River. Localized
changes in the bottom populations were evident in both May, when
no sprinkling occurred, and later in August. The presence of
nearby cattle pastures and septic tank drainage may have
contributed to these changes and made a separation of the effects
of wet decking impossible. Increased algal productivity in
August, probably in part a response to the pastures and septic
tank drainage, may have allowed the bottom animal population to
increase in the downstream reaches. Esthetically, the presence
of Sghaergtilus growths in August, which could not be attributed
solely to wet decking, was a minor problem. Seriously degraded
conditions could happen in this section of river should an
extended period of wet decking occur at a time of low river flow,
especially if there was no dilution by Clear Creek.
STEAMBOAT SLOUGH STUDY SITE
Steamboat Slough study site is on the north side of the Columbia
River about four miles downstream from Cathlamet, Washington.
The slough, approximately 3.2 km long and 90-122 m wide along
most of its length, has a fairly good flow of water. Both ends
of the slough open into a main channel of the Columbia River.
The study site is used for intermittent temporary storage of log
rafts. These rafts may be either spill-over from a nearby log
handling operation or in transit on the Columbia River. No data
were readily available on the amount of recent storage in the
area.
Nine stations were sampled in February and July, 1969 (Fig. 5).
No rafts were in the slough at the time of sampling in February
and only a few were present in July. The bottom materials were
examined at three extra locations in July.
Sand and silty-sand with varying small amounts of bark and
detritus comprised the bottom materials in February and July
42
-------
Station
No.
SB-1
SB-2
SB-3
SB-4
SB-5
SB-6
SB-7
SB-8
SB-9
Station Des c r ip t i on
Steamboat Slough near north bank about
152 meters below upstream end.
Steamboat Slough in mid-channel opposite
station SB-1.
Steamboat Slough near south bank opposite
station SB-1.
Steamboat Slough near north bank about 1036
meters below upstream end.
Steamboat Slough in mid-channel opposite
station SB-4.
Steamboat Slough near south bank opposite
station SB-4.
Steamboat Slough near north bank about 457
meters above downstream end.
Steamboat Slough in mid-channel opposite
station SB-7.
Steamboat Slough near south bank opposite
station SB-7.
COLUMBIA RIVER
Figure 5. Steamboat Slough study site
43
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Table 10. STEAMBOAT SLOUGH STUDY SITE BOTTOM DWELLING ORGANISMS
Station-''
No.
Genera
No./m2
Depth
(m)
Bottom Type
Volume per sample, cc
Bark
Detritus
February 12, 1969
SB-1
SB-2
SB-3,,
SB-4-7
SB-5
SB-6
SB-7
SB-8
SB-9
July 15, 1969
SB-1
SB-2
SB-3
SB-4
SB-5
SB-6
SB-7
SB-8
SB-9
7
7
6
_
3
5
9
5
5
10
6
9
7
5
4 ,
6
6
4
7,619
3,811
3,434
_
786
7,737
8,837
937
2,412
7,081
303
4,251
1,398
227
1,357
980
270
2,399
3
7.6
5.8
7.6
7.6
7.6
7.6
4
2.7
6.1
4.6
3.7
6.7
7
6.7
7.6
4.6
.9
Silty-sand, detritus
Silty-sand, detritus
Silty-sand, detritus,
Hard
Coarse sand, detritus
Silty-sand, detritus
Sand, detritus, bark
Sand, detritus, bark
Sand, detritus
Silty-sand, detritus,
Silty-sand
Silty-sand, detritus,
Silty-sand, detritus
Silty-sand
Silty-sand, detritus,
Silty-sand, detritu,
Silty sand
Silty-sand, detritus,
bark
, bark
bark
bark
bark
bark
bark
0
0
8
-
10
0
5
5
0
13
0
6
0
0
5
6
0
2
30
15
25
-
10
25
20
2
4
20
0
251
7
0
10
1
0
8
a/ One sample per station
b/ No sample.
-------
(Table 10). Bottom samples in February contained 5-10 cc of bark
and 2-3 cc of detritus. The bark ranged from 0.7-20 mm wide, to
1.4-140 mm long. No sample could be obtained at SB-4. Similar
amounts of bark and detrital material were obtained in July at
the majority of stations. Bark ranged from 2-13 cc and detritus
from 1-20 cc per grab sample. A large amount of detritus, 251
cc, occurred at SB-3. The bark ranged from 3-65 mm wide, to 6-
120 mm long.
Log rafts were moored at SB-5 and SB-6 in July. The bottom
materials examined at three additional locations in this area did
not differ from the materials at the regular stations. During
both seasons there was less bark and detrital material at mid-
channel than near the sides of the slough, a probable response to
scouring by the current. The water action plus the limited log
rafting are the most likely causes of the small amount of bark
deposited throughout the slough.
Bottom depths ranged from 2.7-7.6 m in February and from 0.9-7 m
in July (Table 10). The water was slightly murky at both
seasons; transparency, as measured with a Secchi disc, increased
from 0.76 m in February to 1.2 m in July
The chemical water guality did not appear to have adversely
influenced the distribution of the bottom dwelling populations
(Table 11). Dissolved oxygen was high at both seasons and
averaged over 10 mg/1 in February and over 13 mg/1 in July. FBI
was very uniform in February, ranging from 4.8-5.5 mg/1. COD
ranged from 9-10 mg/1 in July. Relatively higher values of COD,
color, turbidity and SS at SB-6 may have been caused by a
localized disturbance of the bottom materials.
The predominant bottom-dwelling animals of Steamboat Slough were
sludgeworms, marine scuds, midge larvae and asiatic clams. The
number of different genera per station ranged from three to nine
in February and from four to ten in July. There was no
relationship between the number of genera and the bottom type
(Table 10, App. E).
In February, the total number of organisms per station averaged
4,447/m2 and ranged from 786-8,857/m2. Populations decreased in
July; the average number per station was 2,030/m2 with a range of
227-7,081/m2. More organisms were collected near the sides than
mid-channel. This was probably a response to increased current
and lesser amounts of bark and detritus in the mid-stream portion
of the slough. The outer stations averaged 6,008 organisms/m2
45
-------
Table 11. STEAMBOAT SLOUGH STUDY SITE WATER CHEMISTRY DATE
Sample
Sta. Depth
No- . fm) .., .
February
Sb-1
SB-2
SB-3
SB-4
SB- 5
SB-6
SB-7
SB-8
SB-9
July 15,
SB-1
SB-3
SB-4
SB-6
SB-7
SB-9
Temp.
°C
12, 1969
3
6.4
5.8
6.4
6.4
6.4
6.4
3.7
2.7
1969
6.T
3.7
6.7
6.7
7.6
.9
2.5
2.5
2.5
3.5
3.5
3.5
3.5
3.5
3.5
19.0
18.5
18.5
18.5
18.5
18.5
DO pH Cond. SS
(mq/1,1) ymho (mq/l)
13.8 6.7 118 21
14.2
14.3 6.7 121 24
13.8 6.4 120 9
13.3
13.6 6.6 117 105
13.6 6.9 118 10
13.6
13.3 6.7 120 34
10.5
10.8
10.4 7.4 138 20
10.4 7.4 138 26
7.2
7.5
VSS Color Turb. FBI COD BOD
tnq/D Pt. Co. Jksn (mq/t (mq/l)Wl'
12 20 12 4.8 8
11
5 15 13 5.3 4
2 30 10 5.1 8
11
9 40 23 5 36
2 25 11 5.1 8
10
3 25 13 5.5 13
10
-
3 5 5 3 10 2
3 15 6 3 10 2
9
9
Ortho
P TKN HO,-N.
> (mq/D tnq/l) ImqVl)
.016 0.7 0.33
.027 0.3 0.42
.036 0.3 0.42
.016 0.7 0.33
.03 0.4 0.44
.025 0.2 0.4
.01 0.3 0.05
.01 0.3 0.06
Note: DO concentrations at the surface were within 1.0 mg/1 of the concentrations observed near the bottom
at each "station.
-------
and mid-channel stations l,845/m2 in February. The average
values for July were 2,911/m2 at the outer stations and only
267/m2 at the mid-channel stations (Table 10) .
Either scuds or sludgeworms were predominant at every station
during both seasons with but two exceptions. In July, midge
larvae comprised 75 percent of the population at SB-2 and asiatic
clams comprised 40 percent at SB-8. No detritus or bark were
present at these two mid-channel stations at this time. Scuds
comprised 37 to 84 percent of the bottom dwelling animals where
they were the predominant forms; sludgeworms made up 43 to 95
percent at stations where they were predominant. There was no
relationship between these latter two animals and the varying
amounts of either bark or detritus (Table 10, App. E).
The bottom-dwelling animals of Steamboat Slough were not
adversely afffected by the small amount of bark deposition.
While there were smaller numbers of organisms at stations with
less bark and detritus, there was no correlation between the
amount of these materials and the type of predominant organisms
with the exception of only two instances in July.
The results from this study site indicate that minimal effects
upon the bottom-dwelling animals could probably be expected from
temporary storage of log rafts in an area subjected to a large
flow of fairly good quality water.
ELOCHOMAN AND CATHLAMET SLOUGHS STUDY SITE
Elochoman and Cathlamet sloughs study site is on the north side
of the Columbia River just downstream from Cathlamet, Washington.
It includes Cathlamet Slough and a portion of Elochoman Slough
(Fig. 6). Log handling and storage activities take place in
Cathlamet Slough and on adjacent land on the north shore. Logs
brought in by raft and truck are graded, sorted, stored in wet
decks, and ultimately transported elsewhere, primarily by log
raft, for use or resale. Approximately 260,000 m3 are handled
annually. In 1968 hemlock comprised about 72 percent of the
total, with the remainder consisting of spruce, cedar, alder, fir
and silver fir.
A crane is used to remove and place logs in the water; they are
lowered rather than being dumped. Most logs are banded into
bundles by steel bands primarily to give greater capacity to the
rafts, but also to prevent sinking and breakage. Accumulated
47
-------
NOTE: Not to scale.
Some log rafting near
S. bank of Cathlamet Slough.
CO
Elochoman Slough
Log Loading and
Unloading Area
COLUMBIA RIVER
afting Area
Figure 6. Elochoman and Cathlamet Sloughs study site
-------
bark is dredged from the log loading areas approximately every 2-
3 months. The bark was removed in May prior to sampling in July,
1969. About every 4-5 years Cathlamet Slough is dredged down to
sand where needed. It was last dredged prior to this study during
the winter of 1967-68. Elochoman Slough is limited to temporary
storage of log rafts.
Elochoman Slough and Cathlamet Slough are each about 2.4 km long
and 60-120 m wide. Water depths are influenced somewhat by tidal
fluctuations in addition to seasonal variations in the river
level. Salt water does not intrude this far upstream. Although
current velocities were not measured in the sloughs, they appear
to be considerably less than in the main channels of the Columbia
River.
Twelve stations were sampled in Elochoman and Cathlamet Sloughs
in February, 1969 (Fig. 6, Table 12). These same stations, with
the exception of EC-8, EC-9 and EC-10, were also sampled in July.
EC-1 was established in the Columbia River near the entrance to
Cathlamet Slough in July. The bottom materials were examined at
four extra locations in July in addition to the regular stations.
Combinations of sand and silt with varying amounts of bark and
detritus comprised the bottom materials of the study site (Table
13). Bottom samples collected in February contained from 0-110
cc of bark and from 7-320 cc of detritus. The bark ranged in
size from 0.7-60 mm wide, to 1.4-125 mm long. No quantitative
samples could be obtained at EC-7 and EC-13. In July, the
samples contained from 15—190 cc of bark and from 15-210 cc of
detritus. The bark ranged in size from 4-50 mm wide, to 6-300 mm
long. There were no large bark deposits within the study area.
The bottom materials from four additional locations in Cathlamet
Slough did not differ from the materials at the regular stations.
Bottom samples were collected from depths of 0.9 - 4.6 m in
February and from 2.7 - 4.9 m in July (Table 13). The water was
slightly murky at both seasons; transparency, as measured with a
Secchi disc, increased from 0.76 m in February to 1.37 m in July.
Floating bark chunks were frequently observed in July.
Dissolved oxygen was high at both sampling seasons, ranging from
9.8-13.8 mg/1. There was little difference in levels of chemical
constituents throughout the study site at each season. In July,
the values were essentially the same in the slough as in the
Columbia River at EC-1 (Table 14).
49
-------
Table 12. SAMPLING STATIONS ELOCHOMAN AND CATHLAMET SLOUGHS STUDY SITE
Station ~ " ~~~~
No. Station Description
EC-1 Columbia River about 152m downstream from the upstream tip of
the island and about 23m from bank of island.
EC-2 Cathlamet Slough about 152m downstream from the tip of the
island. Near N. bank and just upstream of log rafting area.
EC-3 Cathlamet Slough near mid-channel and opposite station EC-2.
EC-4 Cathlamet Slough near S. bank and opposite station EC-2.
EC-5 Cathlamet Slough near N. Bank and immediately downstream
from log loading and unloading area.
EC-6 Cathlamet Slough near mid-channel and opposite station EC-5.
EC-7 Cathlamet Slough near S. bank and opposite station EC-5.
EC-8 Near S. bank of small island at confluence of Elochoman River,
Elochoman Slougn, and Cathlamet Slough.
EC-9 Near mid-channel opposite station EC-10.
EC-10 Near S. bank of channel opposite station EC-10.
EC-11 Elochoman Slough near N. bank about 914m upstream from
mouth of slough.
EC-12 Elochoman Slough near mid-channel and opposite station EC-11.
EC-13 Elochoman Slough near S. bank and opposite station EC-11.
50
-------
Table 13. ELOCHOMAN AND CATHLAMET SLOUGHS STUDY SITE BOTTOM DWELLING ORGANISMS
Station^
No.
Genera
No
./m2
Depth
m
Bottom Type
Volume per
Bark
sample, cc
Detritus
February 11, 1969
EC-2
EC-3
EC-4
EC- 5
EC-6 . .
EC-7 -'
EC-8
EC-9
EC-10
EC-11
EC-12 b/
EC-13 -
July 14, 1969
EC-1 -f
EC-2
EC-3
EC-4
EC-5
EC-6
EC-7
EC-11
EC-12
EC-13
5
3
7
12
4
-
10
11
5
10
8
-
5
9
4
6
4
8
8
11
6
7
10
6
13
28
1
16
13
13
2
11
10
6
13
20
5
4
1
2
,212
,349
,311
,472
,669
-
,098
,452
281
,914
,714
-
722
,030
,219
,834
,636
,025
,210
,241
,043
,669
3
4.
3.
3.
4.
3
.
1.
4.
2.
3.
2.
5.
4.
4.
2.
4.
4.
4.
3
3
3
Silt, detritus, bark
6
7
4
3
9
5
3
1
1
4
2
6
6
7
9
9
6
Sandy-silt,
Sandy-silt,
detritus,
detritus,
bark
bark
Silt, detritus, bark
Silty-sand,
Sandy-silt,
Sandy-silt,
Silty-sand,
detritus,
detritus,
detritus,
detritus,
bark
bark
wood
wood
Sand, detritus, bark
Silty-sand,
Silty-sand,
detri tus ,
detri tus ,
bark
bark
110
21
7
80
70
-
0
0
3
20
20
7
12
100
320
50
-
95
60
3
45
45
Sand, detritus, bark
Silty-sand,
Silty-sand,
Silty-sand,
Silty-sand,
Silty-sand,
Silty-sand,
Silty-sand,
Silty-sand,
Silty-sand,
Silty-sand,
detritus,
detritus,
detritus,
detritus,
detritus,
detritus,
detritus,
detritus,
detritus,
detritus,
bark
bark
bark
bark
bark
bark
bark
bark
bark
bark
15
30
15
95
70
40
190
150
25
no
80
70
55
80
150
210
70
65
15
19
—' One sample per station.
— No sample.
— Columbia River.
-------
Table 14. ELOCHOMAN & CATHLAMET SLOUGHS STUDY SITE WATER CHEMISTRY DATA
en
ro
Sample
Sta. Depth
No. (m;
February 11-12,
EC-3
EC-6
EC-9
EC-12
July 14
EC-1
EC-1
EC-3
EC-6
EC-12
EC-12
4.6
4.3
1.2
3
, 1969
5.2
Sample
4.6
4.9
2.7
Sample
Temp. DO pH
°C (mg/n
1969
3.0
3.0
5.0
3.0
19.0
collected
18.5
18.5
19.0
12.4
13.4
11.6
13.8
9.8
on July
10.1
9.8
9.8
6.7
6.. 8
6.5
6.5
7.4
15
6.5
7.0
7.4
Cond.
ymho
124
126
43
108
130
131
130
130
SS
(mq/1)
10
20
50
18
8
20
21
10
VSS Color Turb.
(ma/1) Pt. Co. Jksn
4 25
5 25
9 50
5 30
1 15
3 15
<1 20
1 10
8
10
22
10
6
7
7
10
PBI COD BOD
4.2 4
3.9 <1
3.2 <5
4.4 5
2 5 1
2 13 2
2 15 1
3 2
Ortho
P TKN N03-N
fran/1) (mq/1) (mn/1 )
\ "»»jf — • i - - \ "*3P* •
-------
The predominant bottom-dwelling organisms of Cathlamet and
Elochoman Sloughs were sludgeworms, marine scuds, asiatic clams,
and midge larvae. The average number of organisms per square
meter was 10,647 in February and 8,323 in July (Table 13, App.
F) .
The bottom populations indicated degradation at stations EC-2 to
EC-7 and better conditions at stations EC-8 to EC-13. No rafts
were present at the time of sampling at stations EC-2 to EC-4.
Log loading and unloading and raft construction and storage were
concentrated in the area near stations EC-5 to EC-7. The areas
near stations EC-8 to EC-13 were not used for rafting.
Sludgeworms, often common inhabitants of areas subjected to
organic enrichment or pollution, comprised 96 to 98 percent of
the organisms at the stations in Cathlamet Slough in February and
from 94 to 98 percent in July. Improved conditions at stations
EC-8 to EC-10, sampled only in February, were indicated by
populations comprised of 54 to 70 percent sludgeworms, 19 to 20
percent scuds and 7 to 14 percent midge larvae (Table 13, App.
F).
The biologically degraded section of the study site had fewer
kinds of organisms, higher populations, and more bark and
detritus than the lower reaches. In February a comparison of the
average values between the five degraded upstream stations and
the five improved downstream stations showed that the genera
increased from six to nine per station, and the number of
organisms decreased from 12,040 - 9,286 per m2. The volume of
bark decreased from 58 - 0.6 cc per sample, and the volume of
detritus decreased from 98 to 56 cc per sample.
The smaller amounts of detritus and generally smaller amounts of
bark in the biologically improved downstream area strongly
suggests that the log handling activities in the upper reaches
have had an adverse effect upon the bottom-dwelling animals. It
seems likely that the larger amounts of detrital material in the
upstream reaches were contributed to in large part by the
unloading, loading, and rafting activities. Decomposition of the
bottom materials at the upper stations probably produced a
habitat more conducive to the establishment of animal populations
tolerant to organically enriched conditions.
A municipal sewage lagoon in the town of Cathlamet just upstream
from the entrance of Cathlamet Slough may have partially
contributed to the degraded conditions of the upper portion of
53
-------
the study area. It was unlikely that the intermittent discharge
from the lagoon would always flow into the slough but the
possibility of some organic pollution from this source does
exist. The results of this study suggest that log rafting
activities in a comparatively sluggish slough can adversely
affect the populations of bottom-dwelling animals.
COAL CREEK SLOUGH STUDY SITE
Coal Creek Slough study site is on the north edge of the Columbia
River downstream from Longview, Washington. It includes most of
Coal Creek Slough, which is used for log storage, and a small
portion of Solo Slough. Log rafts extended along most of the
length of the former slough during sampling in July, 1969; there
were some wet decks in this area also. Approximately 190,000-
212,000 m3 of logs in rafts pass through the slough annually.
Average storage time is about four months for the rafts and about
one year in the wet decks. Douglas-fir make up about 60 percent
of the logs with western red cedar the remainder.
Coal Creek Slough is about 9 km long and 30-122 m wide. Coal
Creek flows into the slough near its upper end. There are two
pumping stations that pump from adjacent low-lying lands into the
slough. One of the stations is located at the upstream end of
the slough and the other about one-third of the distance upstream
from the slough's mouth. The pumps work intermittently; on the
day samples were collected they were not operating. Water in the
ditches leading to the downstream pump station was highly turbid.
Cattle pastures are located adjacent to some of the drainage
ditches.
Nine sampling stations were established at this site (Fig. 7,
Table 15). Six were located in Coal Creek Slough in heavily
rafted areas; three were located upstream in Solo Slough, a non-
rafted area. The bottom materials were examined briefly at six
additional locations.
Virtually stagnant water, low levels of dissolved oxygen and
bottom-dwelling animals tolerant of enriched or polluted
conditions were common throughout the study site. Extensive bark
deposits characterized Coal Creek Slough and were absent from
Solo Slough.
The bottom of Solo Slough was silty and contained from 60 - 120
cc of detritus per sample. Silt, organic ooze, detritus and bark
54
-------
en
CREEK
N
SLOUGH
North Bank
NOTE: Not to scale.
Bends and most branches
in slough not shown.
Figure 7. Coal Creek Slough study site
-------
Table 15. SAMPLING STATIONS COAL CREEK SLOUGH STUDY SITE
Station~Station
No. Description
C-l Solo Slough near E. bank about 7.9 km above mouth of Coal
Creek Slough. About .24 km south of where highway crosses
Coal Creek Slough.
C-2 Solo Slough in mid-channel opposite station C-l.
C-3 Solo Slough near W. bank opposite station C-l.
C-4 Coal Creek Slough near N. bank about 6.4 km above mouth.
C-5 Coal Creek Slough in mid-channel opposite station C-4.
C-6 Coal Creek Slough near S. bank opposite station C-4. In gap
between log rafts.
C-7 Water surface in gap between logs in a raft of cedar logs
located near station C-6.
C-8 Coal Creek Slough near N. bank about 7.2 Km above mouth.
C-9 Coal Creek Slough near mid-channel opposite station C-8.
C-10 Coal Creek Slough near S. bank opposite station C-8.
C-ll Water surface in a gap between logs in a raft of Douglas-fir
logs located near station C-10.
56
-------
comprised the bottom at most of the stations in Coal Creek Slough
(Table 16). Large pieces of bark frequently prevented the Ponar
grab from closing and obtaining a quantitative sample. Bark
which remained in the dredge ranged from 5 - 50 mm wide to 25 -
450 mm long. The bottom materials were examined at six locations
throughout the length of Coal Creek Slough in addition to the
regular sampling stations. Bark and wood fragments were common
throughout the study area. Strands of cedar bark up to six feet
long and small gobs of natural resin were frequently encountered
in the lower reaches of the slough.
The water was 2.7 m deep in Solo Slough and ranged from 3.4 to
10.4 m deep in Coal Creek Slough (Table 16). No flow was
observed throughout the study site and the water was dark and
murky. Transparency, as measured with a Secchi disc, was 1.4 m
in Coal Creek Slough.
Dissolved oxygen was low, averaging about 5 mg/1 in Solo Slough
and only 3 mg/1 in Coal Creek Slough. The values in the latter
slough were below those considered marginal for a healthy aquatic
community. Other chemical constituents varied little throughout
the site. The COD averaged over 24 mg/1, higher than at the
other log rafting sites (Table 17).
The predominant bottom-dwelling animals in both sloughs were
sludgeworms, common inhabitants of enriched or polluted
environments. They comprised 95 to 98 percent of the
approximately 3,268 organisms/m2 in Solo Slough. In Coal Creek
Slough they made up 93 to 96 percent of the 5,531 to 8,597
organisms/m2 at C-5 and C-6 and appeared to be the predominant
animals in the non-quantitative samples (Table 16, App. G) .
Solo Slough, not subjected to log rafting, did not seem to be of
any better quality based on kinds and numbers of bottom-dwelling
organisms than heavily rafted Coal Creek Slough. Degraded
biological conditions were apparent in both sloughs. Since only
stations C-5 and C-6 in Coal Creek Slough could be sampled
quantitatively, precise comparisons between the bottom
populations and bark deposits of the two sloughs were not
possible. The low level of dissolved oxygen in Solo Slough was
very likely influenced by the extensive bark deposits in Coal
Creek Slough. The predominance of sludgeworms in both sloughs
was a probable response to these low oxygen levels.
The lack of flow throughout the study area was certainly a major
contributing factor to the degree of pollution. Tidal
57
-------
Table 16. COAL CREEK SLOUGH STUDY SITE BOTTOM DWELLING ORGANISMS
en
oo
Station^
July 16, 1969
C-l
C-2
C-3
C-4&/
C-5
C-6
C-8^
C-9&/
C-10&/
No. No./m2
Genera
3 3,369
4 3,088
3 3,347
4
4 5,531
6 8,597
3
6
5
Depth
m
2.7
3
2.7
3.4
6.4
6.1
6.7
10.4
6.7
Bottom Type Volume per sample, cc
Bark Detritus
Silt, detritus 0 62
Silt, detritus 0 120
Silt, detritus 0 120
Silt, ooze, detritus ,-
bark
Silt, ooze, detritus, 25 90
bark
Silt, ooze, detritus, 90 70
bark
Hard
Silt, ooze, detritus,
bark
Silt, ooze, detritus,
bark
a/
One sample per station.
-/ Non-quantitative sample only.
-------
Table 17. COAL CREEK SLOUGH STUDY SITE WATER CHEMISTRY DATA
Sample Ortho
Sta. Depth Temp. DO pH Cond. SS VSS Color Turb. PBI COD BOD P TKN NO,-N
No. m °C (mg/1) ymho (mg/1) (mg/1) Pt. Co. Jksn (mg/1) (mg/1) (mg/1) (mq/D (mg/1) (mg/1)
July 16, 1969
C-2 0 19.0 5.7
C-2 2.7 19.0 4.7 6.9 257 16 4 50 12 <1 27 2 .011 0.8 .09
C-4 0 21.0 3.6
C-4 3.4 19.0 3.6 6.8 227 14 3 50 10 <1 20 2 .019 0.9 .1
C-6 0 20.0 3.9
C-6 6.1 18.5 3.7 6.8 232 52 6 50 22 3 26 1 .021 0.8 .1
C-7 0 36
C-8 0 20.0 3.0
C-8 6.7 19.0 2.4 17
C-10 0 20.0 3.0
C-10 9.8 19.0 1.6 22
C-ll 0 22
-------
fluctuations in the Columbia River probably resulted in some back
and forward movement of water but its diluting effects would have
been minor. Since the oxygen demand exerted by the decomposing
bark was not satisfied by fresh water coming from upstream, it
consequently lowered what little oxygen was available in the
immediate area. The lower dissolved oxygen levels and organic
ooze in the bottom deposits of Coal Creek Slough demonstrate an
aspect of damage to the aquatic environment by extensive bark
deposits.
MULTNOMAH CHANNEL STUDY SITE
Multnomah Channel study site is on the western edge of the
Multnomah Channel near Scappose, Oregon. The site includes a
raft make-up area and a raft storage area. Logs are hauled to
the site by truck, lowered into the water by a crane, graded,
sorted, and grouped into rafts. Smaller logs are banded into
bundles. About 47,000 m3 are handled annually. There are raft
storage areas scattered along both shores upstream and downstream
from the study site; however, the total amount of log handling in
Multnomah Channel was not determined.
Multnomah Channel is part of the Willamette River. It branches
off from the main channel about 3.2 km upstream from the mouth
and flows into the Columbia River at St. Helens, Oregon. The
channel is about 3t km long and about 122 - 305 m wide. Tidal
action extends this far upstream. A computer study of the
Columbia River shows that under some low flow conditions the flow
in Multnomah Channel would be reversed during high tide (Callaway
1970). Waste discharges to the Willamette River in the Portland-
Oregon City area have some effect on water quality in Multnomah
Channel. No attempt was made during this study to evaluate the
changes in water quality due to these other waste sources. Six
stations were established within and near the log unloading and
rafting area and were sampled in August, 1969 (Fig. 8).
The bottom of the Multnomah Channel in the study area was
basically silty-sand (Table 18). Bark and detritus deposits were
also present within the unloading and raft make-up area but only
small amounts of bark were collected at M-6 across the channel.
Downstream from the unloading area at M-5 the bottom was very
hard; no sample could be collected. Some bark, 150 cc, was in
the bottom sample collected in the immediate unloading area at M-
2. Downstream from this station at M-3, 270 cc of bark were
collected. This increase was probably due to water current, both
natural and that set up by the unloading of the bundled logs.
Detrital material, equal in volume to the amount of bark at these
60
-------
Station
No.
M-l
M-2
M-3
M-U
M-5
M-6
Station Description
Multnomah Channel near west bank about
lUO-l8o meters upstream from log unloading
area.
Multnomah Channel at log unloading area.
Multnomah Channel about 25 meters from west
bank and 75 meters downstream from log
unloading.
Across the channel from Station M-2.
About 15 meters from east bank.
Multuomah Channel near west bank approximately
.5 km below log unloading area.
Across the channel from Station M-5.
About 15 meters from east "bank.
N
Note: Not to scale.
Curve in channel not shown.
Log Unloading Area
•Raft Makeup Area
MULTNOMAH
w^
CHANNEL
Figure 8. Multnomah Channel study site
61
-------
Table 18. MULTNOMAH CHANNEL STUDY SITE BOTTOM DWELLING ORGANISMS
rv>
Station^
2
No. No./m Depth Bottom Type Volume per
Genera m Bark
sample, cc
Detri tus
August 12, 1969
M-l
M-2
M-3
M-4
H-sfe/
M-6
1 560 5.5 Silty-sand 0
3 431 2.1 Silty-sand, gravel, 150
detritus, bark
. 8 5,145 5.8 Sandy-silt, gravel 270
detritus, bark
3 474 9.8 Sandy, detritus 0
12.2 Hard
5 2,292 7.6 Silty-sand, detritus, 6
bark
90
160
250
22
-
5
—' One sample per station
—' No sample
-------
two stations, was probably associated with the logging activities
since very little of it was found upstream or across the channel.
The bark collected in the samples ranged from 40-55 mm wide and
from 6-150 mm long. Small amounts of natural resin were found in
the bottom materials at each station except M-5. Gas bubbles,
presumably from anaerobic decomposition, were observed on a
reconnaissance survey in October, 1968.
The water was only 2.1 m deep at the unloading area and increased
to 12.2 m at M-5 (Table 18). Transparency, as measured with a
Secchi disc, was 0.91 m. The water, murky at all stations, was
characterized by a piney or resinous odor in the vicinity of the
unloading area.
Chemical water quality was fairly uniform at all stations.
Dissolved oxygen was somewhat low (5.1-5.3 mg/1), near the
marginal level for a healthy balanced aquatic community.
Organics were also low as indicated by the COD (9-11 mg/1) and
BOD (1-2 mg/1) concentrations. Suspended solids ranged from 16-
28 mg/1 and were mainly inorganic (Table 19).
The poor water quality of the Multnomah Channel was reflected by
the predominance of sludgeworms at each station (App. H). These
organisms, often associated with enriched or organically polluted
conditions, comprised from 93 to 100 percent of the population at
stations M-l, M-2, M-3 and M-6. Slightly better quality was
indicated across the channel at M-4 where scuds made up 20
percent and sludgeworms 77 percent of the population. However,
M-6, also across the channel, had 93 percent sludgeworms.
Station M-3, with 5,145 organisms/m2, had from two to ten times
more organisms than the rest of the stations. Although more
variety was indicated by the eight different genera present here,
serious degradation was still shown by the sludgeworms which
comprised 94 percent of the population. The larger amounts of
detritus at this station probably represented a habitat more
conducive to increases in numbers and variety than did plain,
silty-sand bottom materials (Table 19) .
Water quality in this section of the Multnomah Channel was
degraded/ particularly biologically. Bark deposits were not
extensive and were generally limited to the unloading and rafting
area. However, the bottom dwelling organisms indicated
degradation was common even across the channel from the handling
activities. The small number of samples collected were
inconclusive as to whether conditions were better or worse within
63
-------
Table 19. MULTONOMAH CHANNEL STUDY SITE WATER CHEMISTRY DATA
cy>
Sample
Sta. Depth Temp. DO pH
No. m °C
-------
or outside of the unloading area. There is little doubt that if
the entire channel contained extensive bark deposits with their
subsequent smothering action and anaerobic decomposition, the
presently degraded conditions would only worsen.
SIUSLAW RIVER STUDY SITE
Siuslaw River study site extends from Mapleton, Oregon, to about
7.6 km downstream. Just downstream from Mapleton there is a
sawmill, stud mill and a plywood mill. Logs are stored in wet
decks and when needed are debarked and placed in the water along
the north bank. Peeler cores from the plywood mill are
temporarily stored in the river until used in the stud mill.
About 142,000 m3 of logs are handled annually, mainly fir with
some hemlock.
There is another sawmill about 7.2 km downstream from Mapleton.
Logs are trucked to this sawmill, dumped into the river, grouped
into rafts and stored until needed. The raft storage area
extends about 1.6 km upstream and 21 km downstream from the
sawmill. Approximately 70,000 m3 of logs, consisting of 85
percent fir, 10 percent hemlock, and 5 percent cedar, are handled
annually. The inventory of logs in storage is usually about
12,000 m3, but may go as high as 21,000 m3.
The Siuslaw River drains an area of 2,002 ha and flows into the
Pacific Ocean. Most of the area upstream from the study site is
forested. Precipitation in the area varies from 101 to 254 cm.
Duringlow flow in the summer, salt water intrudes as far upstream
as Mapleton, 32 km from the ocean. Domestic waste disposal at
Mapleton, population 700, is by septic tanks. There does not
appear to be any significant waste discharges upstream from the
town.
The Siuslaw River is a good coho salmon, steelhead and cutthroat
trout producer. It also has a good fall chinook run. Most of
the fish production occurs in the tributaries since these have
lower summer water temperatures and greater quantities of
spawning gravel (OSWRB 1965).
Ten sampling stations established in log dumping and rafting
areas were sampled during September, 1969 (Fig. 9, Table 20).
65
-------
NOTE: Numerous log rafts tied along the river
are not shown in the diagram below.
Bridge
SIUSLAW RIVER
/Lo
n\
XlC
lorth
Bank
Mill
g Holding
Area
/
Log Dump \Mill
10)
Figure 9. Siuslaw Rivervstudy site
-------
Table 20. SAMPLING STATIONS SIUSLAW RIVER STUDY SITE
Station'Station
No. Description
S-l Siuslaw River approximately 0.8 km upstream from bridge.
S-2 Siuslaw River near N. bank about 0.8 km downstream from bridge.
S-3 Siuslaw River near N. bank about 3.2 km downstream from bridge.
S-4 Across river from station No. S-3.
S-5 Si us!aw River near N. bank about 4 km downstream from bridge.
In gap between two log rafts.
S-6 Across river from station S-5. In gap between two log rafts.
S-7 About 6.4 km downstream from bridge. In gap between two log
rafts.
S-8 Siuslaw River about 7.2 km downstream from bridge. About 22.8
m downstream of log dump on N. bank.
S-9 Across the river from station S-8.
S-10 Siuslaw River near N. bank about 7.6 km downstream from bridge.
About 180-275 m downstream from mill.
S-ll Across the river from station S-10.
67
-------
The bottom of the Siuslaw River study area was mainly silty-sand
with varying amounts of bark and detritus (Table 21). Although
no large bark deposits were observed, no station where a sample
could be collected was without some bark. A hard bottom
prevented quantitative sample collecting at S-4 and S-ll. Ooze,
with an odor typical of anaerobic decomposition, was the
predominant material at S-8 near the log dump. This sample also
contained 215 cc of bark, almost 3 to over 40 times as much as at
the other locations. The bark at all the stations combined
ranged in size from 4-40 mm wide, to 10-200 mm long. Natural
resin was found in samples at S-2, S-5, S-6, S-8, and S-10. The
samples at stations S-3 to S-7 contained from 8-50 cc of detrital
material while about 200 cc were collected at stations S-8 to S-
10.
Transparency, as measured with a Secchi disc, was about 1.8 m
throughout the study area. The water was 7.9 m deep at S-8 near
the log dump; depths at the other stations ranged from 3.4 to 4.6
m (Table 21). Numerous bark chunks were floating on the surface
throughout the area.
Dissolved oxygen was low throughout the study site(4.5-6.3 mg/1)
and tended to be marginal for a healthy aquatic community
upstream at station S-l. There was little difference in oxygen
concentration from the surface to the bottom at several of the
stations. Color, turbidity, FBI and nitrogen were all fairly
uniform. COD ranged from 6-8 mg/1 at most of the stations and
was at 12 and 26 mg/1 at stations S-l and S-10, respectively.
Salt water intrusion was reflected in the increase in chlorides
as the river progressed downstream. Chlorides in the upper
reaches were about 10 percent of that expected in the ocean;
values in the lower reaches were about 25 percent (Table 22).
Station S-2 was upstream from a section of the river used for
barked log storage; station S-3 was just downstream from this
area (Figure 9). The bottom was degraded at both locations as
indicated by the high percentage of sludgeworms, about 98 percent
of the 21,016 and 10,342 organisms/m2 at these two stations,
respectively (App. I). Slightly better conditions may have
existed at S-2, however. Ten different genera were collected at
this station and only five at S-3. This increased variety may
have been a response to the larger amounts of detritus at the
upstream station. One hundred fifty cc of detritus were in the
sample from S-2, five times as much as at S-3. Bark deposits at
both stations were minimal. Station S-4, across the river from
S-3, could not be sampled quantitatively (Table 21).
68
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Table 21. SIUSLAW RIVER STUDY SITE BOTTOM-DWELLING ORGANISMS
to
Station a/
No.
Genera
No./m2
Depth
Bottom Type
(m)
Volume per sample, cc
Bark
Detritus
September 12, 1969
S-2
S-3
S-4 b/
S-5
S-6
S-7
S-8
S-9
S-10
S-ll c/
10
5
3
5
5
6
6
9
12
"
21,
10,
-
10,
4,
2,
5,
7,
12,
016
342
_
276
197
486
079
232
904
3.
3.
3.
3.
3.
3.
7.
3.
4.
4.
4
7
7
7
7
7
9
7
6
6
Silty-sand,
Silty-sand,
Hard
Silty-sand,
Silty-sand,
Silty-sand,
Ooze, silt,
Silty-sand,
Silty-sand,
Hard
detritus
detritus
gravel ,
gravel ,
detritus
detritus
detritus
detritus
, wood, bark
, wood, bark
detritus, wood, bark
detritus, wood, bark
, bark
, bark
, bark
, bark
15
5
—
8
14
80
215
40
12
150
30
—
50
8
9
200
210
210
&/ One sample per station.
b/ Non-quantitative sample.
c/ No sample.
-------
Table 22. SIUSLAW RIVER STUDY SITE WATER CHEMISTRY DATA
Sta.
No.
Time
PBT
Sample Temp. DO Cl Color
Depth m. °C (mg/1) pH (mg/1) Pt. Co.
September 10, 1969
S-l
S-2
S-3
S-3
S-4
S-4
S-8
S-8
S-9
S-10
S-ll
1040
1010
1115
1120
1135
1140
1335
1340
1350
1410
1425
4
3
3
0
3
0
7.3
0
3
3.4
4.6
20.5 4.5
20.0 5.1
20.0 5.8
20.0 6.3
5.2
5.9
20.5 5.9
5.9
5.9
20.5 6.2
6.4
6.5 1790 15
6.7 1960 15
6.5 2100 15
6.4 4820 15
6.4 4620 15
6.8
6.4
Turb. FBI COD BOD
Jksn (mq/lKmci/1) (mo/1)
12
4 2 8 <1
3 2 6 <1
5262
41 6 <1
5151
26
6
Ortho-P TKN N03-N
fma/1) (ma/1) fma/M
.002 0.4 .02
.003 0.5 <,02
.01 0.4 <.02
.04 0.4 .02
Tide appeared to be coming in throughout the time of sampling. In a mixture of fresh and ocean water
the solubility of oxygen decreases as the salinity increases. With zero chloride concentration the
solubility is 9.2 mg/1 at 20°C as compared to 8.7 at a chloride concentration of 5,000 mg/1.
-------
Stations S-5 and S-6, on opposite sides of the river from each
other, were both adjacent to log rafts (Fig. 9) . Sludgeworms
comprised from 94 to 98 percent of the bottom dwelling animals at
both locations. Total populations ranged from 10,276/m2 at S-5
to 4,197/m2 at S-6. Only five genera were collected from each of
these staions. There were 50 cc or less of detritus and up to 14
cc of bark in the samples collected here (Table 21, App. I).
Station S-7 was farther downstream in a rafting area (Fig. 9).
Only slightly over 2,475 organisms /m2 were collected here,.
Sludgeworms comprised only 19 percent of the bottom animals while
a type of scud common in marine waters made up 48 percent. This
sudden decrease in Sludgeworms is difficult to explain since the
bottom type was not essentially different from station S-6
upstream. The large increase in scuds may have been a response
to increasing salinity (Table 21, App. I) .
Degraded conditions were evident at S-8, just downstream from a
log dump (Fig. 9). Sludgeworms comprised 77 percent of the
bottom-dwelling animals, pollution-tolerant red midge larvae 12
percent and scuds only 3 percent. The amount of bark in the
sample at this station was 215 cc, while across the river at S-9
there were only 40 cc. Slightly better conditions at S-9 may
have been indicated by a small decrease in the percentage of
Sludgeworms to 70 percent and an increase in scuds to 12 percent.
No red midge larvae were collected here. Total numbers of
organisms ranged from 5,079/m2 at S-8 to 7,2327 mz at S-9 (Table
21, App. I).
Station S-10 was on the same side of the river and downstream
from S-8 in an area free from log rafts (Fig. 9). Over 12,900
organisms/m2 were collected here. Sludgeworms made up only 29
percent of the population, scuds 58 percent and red midge larvae
14 percent. Polychaete worms, usually found in brackish or
marine waters, comprised 6 percent of the animals. Increased
varity and seemingly better quality was indicated by 12 different
genera collected at this station. Only 12 cc of bark were in the
bottom sample from this location; the amount of detritus was the
same as at the two previous stations, about 200 cc. No sample
could be collected across the river at station S-ll (Table 21,
App. I) .
Comparisons between the bottom-dwelling animals of the Siuslaw in
areas subjected to log dumping or rafting to populations in areas
not used for these activities are very difficult. The relatively
small number of samples collected at this study site can only
indicate what conditions actually are and perhaps emphasizes some
71
-------
possible problems. The seemingly better conditions, as indicated
by the bottom dwelling animals, at S-10 may also have been an
indicator of increased salinity in this area of the study site
and not necessarily a response to improved bottom conditions.
Aquatic scuds are commonly associated with good water quality;
however, the scuds in this area of the Siuslaw River were a
marine type, certain species of which can adapt to brackish or
fresh water. Their presence in the lower reaches was a more
probable response to the increased salinity than improved bottom
conditions. These organisms were found with varying amounts of
bark and detritus and were not definitely associated more with
one material or the other.
Most sludgeworms, or oligochaetes , are fresh water forms and are
not generally found in areas subjected to salt water. Their
decrease in the lower reaches and predominance at the upstream
stations was a very probable response in the increasing salinity.
The sludgeworms were also found with varying amounts of bark and
detritus.
The number of different genera per station were related to the
amount of detritus in each sample. Five to six genera were found
in samples with 8 - 50 cc of detritus while 9-12 genera were
found in samples with 150-210 cc of detritus. No such
relationship was apparent between the number of genera and the
amount of bark.
Decomposing bark and other bottom materials could be a cause of
the generally low dissolved oxygen values (U-5 - 6.3 mg/1). In
addition, low river flow accompanied by current reversals due to
tidal action probably prevent a needed constant flushing with
fresh water from upstream. Additional or larger deposits of
decomposing bark on the bottom in this situation could only serve
to worsen conditions and also could be a threat to anadromous
fish migration.
Esthetically, log rafting activities in this section of the
Siuslaw River were responsbile for a reduction in the
recreational value of the stream. Numerous bark chunks and other
logging debris were frequently observed on the surface.
72
-------
SECTION VII
REFERENCES
American Public Health Association, Inc. 1965. Standard Methods
for the Examination of Water and Wastewater, 12th Ed. APHA,
Washington, D.C. 769 p.
Bartsch, A. P. 1960. Settleable solids, turbidity, and light
penetration as factors affecting water quality. In:
Transactions of the Second Seminar in Water Pollution.
Robert A. Taft Sanitary Engineering Center. Cincinnati,
Ohio. April 20-24. 118-127 pp.
Bartsch, A. F. and W. S. Churchill. 1949. Biotic response to
stream pollution during artifical reaeration. In:
Limnological Aspects of Water Supply and Waste Disposal.
American Association for the Advancement of Science,
Washington, D.C. 33-48 pp.
Browning, B. L. (editor). 1963. The Chemistry of Wood. John
Wiley and Sons, Inc., New York.
Callaway, Richard. July 1970. Personal Communication. National
Coastal Pollution Research Program, Federal Water Quality
Administration, Pacific Northwest Water Laboratory,
Corvallis, Oregon.
Dobie, J. 1965. Reduce inventory losses with proper log
storage. British Columbia Lumberman, 49 (4):16-17.
Ellis, M. M. 1943. Stream pollution studies in the State of
Mississippi. U.S. Fish and Wildlife Service, Special
Scientific Report No. 3, p. 13.
Felicetta, Vincent F. and Joseph L. McCarthy. 1963. The Pearl-
Benson or NitrosO, method for the estimation of spent
sulfite liquor concentration in waters. Tappi 46 (6): 337-
347.
73
-------
Graham, Robert D. and Donald J. Miller. 1969. Staining of wood
and its prevention. Forest Research Laboratory, Special
Report No. 2 (revised) Oregon State University, Corvallis.
Hynes, H. B. N. 1960. The biology of polluted water. Liverpool
University Press, Liverpool, England.
Ingram, W. M., K. M. MacKenthun and A. F. Bartsch. 1960.
Biological field investigative data for water pollution
surveys. U.S. Department of the Interior, Federal Water
Pollution Control Administration, Publication WP-13.
Keup, L. E., W. M. Ingram and K. M. MacKenthun. 1960. The role
of bottom-dwelling macrofauna in water pollution
investigations. Public Health Service Publication No. 99-
wp-38.
Klein, L. 1962. River Pollution II. Causes and Effects.
Butterworth•s London.
McHugh, M. J. November 1968. Personal Communication.
Department of Fish and Game, State of Alaska.
McHugh, Robert A., Laverne S. Miller and Thomas E. Olsen. 1964.
The ecology and naturalistic control of log pond mosquitoes
in the Pacific Northwest. Oregon State Board of Health,
Salem.
Mackenthun, K. M. 1969. The practice of water pollution
biology. U.S. Department of the Interior, Federal Water
Pollution Control Administration, Division of Technical
Support, Washington, D.C.
McKeown, J. J., A. H. Bennedict and G. M. Loche. 1968. Studies
on the behavior of benthal deposits of wood origin. Journal
of water pollution control Federation, 40 (suppl):R333-353.
Oregon State Water Resources Board. 1961. Upper Willamette
River Basin. Salem, Oregon.
74
-------
Oregon State Water Resources Board. 1962. John Day River Basin.
Salem, Oregon.
Oregon State Water Resources Board. 1965. Mid-coast basin.
Salem, Oregon.
Phinney, H. K. 1969. Physiological ecology. In: Proceedings of
the Eutrophication-Biostimulation Workshop. University of
California and Federal Water Pollution Control Agency,
Berkeley, California. June 19-21. pp. 141-145.
Schaumburg, Frank D. 1970. The influence of log handling on
water quality. Annual Report (1969-1970) FWPCA Research
Grant WP-01320. Dept. of Civil Engineering, Oregon State
University, Corvallis.
Stein, Jerome E. and John G. Denison. 1966. In situ benthal
oxygen demand of cellulosic fibers. Advances in Water
Pollution Research, Vol. 3. Proceedings 3rd International
Conference on Water Pollution Research.
U.S. Department of the Interior. 1968. Preliminary survey of
fish and wildlife in relation to the ecological and
biological aspects of Yaquina Bay, Oregon Fish and Wildlife,
Portland, Oregon.
U.S. Department of the Interior. 1969. Methods of chemical
analysis of water and wastes. Federal Water Pollution
Control Administration. Analytical Quality Control
Laboratory, Cincinnati, Ohio. 280 p.
Welch, P. S. 1948. Limnological Methods. McGraw-Hill Book
Company, Inc., New York.
Westfall, B. A. 1946. Stream pollution hazards of wood pulp
effluents. U.S. Fish and Wildlife Service, Fishery Leaflet
174. 8 p.
Wright, B. S. 1963. Effect of stream driving on fish, wildlife
and recreation. Pulp and Paper Magazine of Canada,
63(11):WR433-WR439.
75
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-600/2-76-262
2.
4. TITLE AND SUBTITLE
EFFECTS OF LOG HANDLING AND STORAGE ON WATER QUALITY
7. AUTHOR(S)
Gerald S. Schuytema and Robert D. Shankland
9. PERFORMING ORGANIZATION NAME Al\
Food & Wood Products Brand
Corvallis Field Station
200 SW 35th Street
Corvallis. OR 97330
JD ADDRESS
ti, lERL-Cincinnati
12. SPONSORING AGENCY NAME AND ADDRESS
Industrial Environmental Research Lab - cin. - OH
Office of Research and Development
U.S. Environmental Protection Agency
Cincinnati. OH 45268
3. RECIPIENT'S ACCESSION«NO.
5. REPORT DATE
September 1976 (Issue Date)
6. PERFORMING ORGANIZATION CODE
8. PERFORMING ORGANIZATION REPORT NO.
10. PROGRAM ELEMENT NO.
1BB045
11. CONTRACT/GRANT NO.
12-100-EBG
13. TYPE OF REPORT AND PERIOD COVERED
Final Report
14. SPONSORING AGENCY CODE
EPA/600/12
15. SUPPLEMENTARY NOTES
16. ABSTRACT
The biological and chemical effects of three types of log storage on water
quality were investigated. Three flow-through log ponds, two wet deck operations,
and five log rafting areas were studied. Both biological and chemical aspects
of stream quality can be adversely affected by flow-through log ponds and runoff
from wet decks. Severity of degradation varies widely with each situation.
Runoff from wet decks had pollution characteristics equal to or greater than that
of the waters from the flow- through log ponds studied.
Esthetically, a stream can be affected by the dark color of the water coining
from a log pond or wet deck. Floating bark from a log raft or a log pond is also
aesthetically displeasing. The most significant problem associated with log
rafting is the loss of bark which commonly occurs when the logs are dumped into
the water.
17.
a. DESCRIPTORS
KEY WORDS AND DOCUMENT ANALYSIS
b.lDENTIFIERS/OPEN ENDED TERMS
Water Pollution, Sawmills, Lumbering, Log Storage, Log Ponds,
Water Quality, Biological Oxygen Wet Deck Operations,
Demand, Chemical Oxygen Demand, Color Log Rafting
13. DISTRIBUTION STATEMENT
19. SECURITY CLASS (This Report)
UNCLASSIFIED
20. SECURITY CLASS (This page)
UNCLASSIFIED
c. COSAT1 Field/Group
13B
21. NO. OF PAGES
84
22. PRICE
EPA Form 2220-1 (9-73)
76
U.S. GOVERNMENT PRINTING OFFICE: 1977-7 57-056/5499
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