June 1974
Environmental Protection Technology Series
* -5J. j '''-',
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-------
RESEARCH REPORTING SERIES
Research reports of the Office ol Research and
Monitoring, Environmental Protection Agency, have
been grouped into five series. These five broad
categories were established to facilitate further
otevelopwent and, application ' '. of envir<
tectmology. .. . Elinirafcian of traditional
was consciously planned to foster ' "."
transfer and a naxinnui interface ' in re!
-IT i 'i. ' • ,i i.i'. 'I. ~ i. . i i i i - •' . ' '
_ Health Effects Research
1 Protection Technology '
Re
has been assigned to the
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^jpi'Tmr TTOi iT - i •'' i — '
degradation fiow point ai ._. ,-_...- ^ ,,,.- . , -..
pollution. «iis work provides the new or imprdved
technology required for the control and1' treatment
of Dilution sources to «eet environmental quality
standards.
EPA REVIEW HOTICE
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Development, EPA, and approved for publication* Approval
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D.C. 9MB - Price $M5
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EPA-660/2-74-028
June 1971*
BIOLOGICAL TREATMENT OF CONCENTRATED
SUGAR BEET WASTES
By
James H. Fischer
Project 12060 FAK
Program Element 1 BB037
Roap/Task 21 BAB 82
Project Officer
Ralph H. Scott
Pacific Northwest Environmental Research Laboratory
National Environmental Research Center
Corvallis, Oregon 97330
Prepared for
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
-------
ABSTRACT
A study of the variables influencing a closed loop recirculating flume
water system for conveying sugarbeets for processing was conducted
at Longmont, Colorado. The results show that high volume, high
total solids transport (flume) waters can be recirculated with little or
no discharge to receiving waters. Rapid removal of suspended solids
was accomplished by screening, followed by continuous addition of
lime prior to sedimentation. The build-up of total dissolved solids
was no major problem during the operation periods, provided the pH
was 10 or greater and that water temperature did not exceed 20°C.
The system was designed for primary settling in two alternately used
ponds. Settled mud was removed from one pond by clamshell while
the other one was in service. The first settling pond effluent was sub-
jected to secondary settling before returning to the fluming and washing
operations. These segments of treatment essentially operated without
odor.
A deep anaerobic pond designed to degrade remaining solids in the sur-
plus water was effectively used to treat the total system waters at the
end of each operating campaign. Floating surface aerators were used
with success the first year to reduce odor but failed to be consistently
effective the second year. The aerators were effective in helping
final polishing to meet discharge standards.
Biological and nutritional data were collected to evaluate operational
quality, water quality and bio-activity. While the results indicate
that the end product water meets discharge standards,, such treated
wastes were retained for re-use in the system. Further work is
needed on mud handling and odor abatement.
This report was submitted in fulfillment of Project Number 12060 FAK
by the Beet Sugar Development Foundation under partial sponsorship
by the Environmental Protection Agency. Work was completed as of
October 1970.
11
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CONTENTS
Page
Abstract . ii
List of Figures iv
List of Tables v
Section
I Conclusions 1
II Recommendations 3
III Introduction 5
VI Design and Construction 9
V Experimental
General 15
Sample Collection 16
Analytical Procedures 17
VI Discussion
Lime Addition and pH 19
Solids Removal 24
Dissolved Solids, COD, BOD in Recirculated
Water 28
Anaerobic Pond 32
VII Bibliography 47
VIII Appendices, Analysis of data 51
111
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FIGURES
Page
1. Schematic Flow Diagram of L-ongmont Flume System 10
2. Elevated DSM Screens Slowing Manifold and Valve System 11
3. Parshall Flume and Hose Arrangement for Addition of
Milk of Lime 11
4. Aerial Photo of Project Site and Treatment Ponds 13
5. Relation of Dissolved Oxygen to pH at Three
Sampling Points 20
6. The Relation of Lime Addition to pH at the Second
Pond Effluent. The Percent Untreated Return Flow
is Shown 22
7. Trash and Solids Removed by Screening 25
8. SPE Increase in Concentration of Dissolved and
Suspended Solids during Campaign 29
9. SPE Increase in TOG, 300$ and COD during Campaign 30
10. SPE Relationship Between Total Sugars, Organic Acids
and pH during Campaign 31
11. Anaerobic Pond Sampling Points after Campaign,
Sampled at Depths of 3, 6, 9 and 12 Feet 38
12. Effect of Nutrient Addition and the N-P2C>5 Analysis
on Rate of BODc Reduction. The Water Temperature
is also Shown, 1968-69 Campaihn 39
13. Multiple Curves Showing the Average Weekly Analysis
During the Post-Campaign Period of 7 Months 40
IV
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TABLES
No. Page
1. pH and Alkalinity Study FPI Grab Samples, 1968-69
Campaign 21
2. Median pH, FPI, SPE Weekly Average of Grab Samples
Three Times Per Day 23
3. Weekly Mud Composites, 1968-69 Campaign Average 26
4. Change Per Day Across First and Second Ponds
1968-69 Campaign Average 27
5. Nitrogen, Sulfur, and Phosphorus Concentrations,
1968-69 Campaign 32
6. Anaerobic Pond Effluent, 1967-68 Campaign 34
7. Organic Degradation in Anaerobic Pond, 1968-69
Campaign 35
8. Anaerobic Pond During Campaign, 1968-69 Campaign
Average 36
9- Anaerobic Pond; Post Campaign 1967-68, 1968-69;
Reductions 41
10. Anaerobic Pond, September 23, 1969; Final Analysis and
Total Reductions for 1968-69 Post Campaign Period 43
11. Bacteria Counts (weekly average) and Pond Aeration;
Anaerobic Pond 1967-68 Post Campaign 45
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SECTION I
CONCLUSIONS
The principle of total recirculation of sugarbeet factory flume and
wash waters has been proven to be successful. Best results are ob-
tained when adequate quantities of lime, as CaO, are continuously in-
jected into the system at a rate sufficiently high to produce a pH
greater than 10. To maintain a high pH with minimum lime addition,
the system waters should be kept under 20°C.
Under the above conditions, settleable solids can be rapidly concen-
trated into a mud that can be removed in ponds or in a typical clari-
fier. The supernatant can be returned with minimum retention or no
retention to repeat the fluming-washing cycle. The continuous build-
up of dissolved solids does not interfere with the hydraulics but does
aggravate the foaming problem. Odors are not a problem under high
pH conditions.
The loss of system water with the settled mud seems to equal an inherent
make-up. No water needs to be discharged during an operating campaign,
therefore, there need be no concern over water quality from this source.
Removal and handling of settled mud, however, is a continuous problem.
After an operating campaign the system waters are bio-degradable and
can be ponded for re-use as has been done at Longmont for 3 years con-
secutively. None of the methods used to date has accomplished the
degradation process without periods of high odors. A true anaerobic or
aerobic condition was never attained with or without mechanical surface
aeration; a facultative condition existed. However, the residue water
received sufficient treatment to meet discharge quality standards even
though the time required exceeded expectations.
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SECTION II
RECOMMENDATIONS
The Longmont waste water treatment system, with modifications, is
recommended for use in geographical areas where the system waters
do not exceed 20°C. Higher temperatures increase fermentation rates
and lime requirements. Even then, the liming principle does have
application as an economic aid to-hasten settling of solids.
Two main problems remain to be solved. It is recommended that
further research be conducted on the dewatering and transport of settled
mud. Odor production from settled mud in ponds continues for prolonged
periods of time. Standard methods of dewatering are either too costly
or do not perform to satisfaction under normal conditions.
Further research is recommended on the treatment of end of campaign
residue water. The anaerobic or facultative methods of treatment pro-
duce unpleasant odors. Several types of aerobic systems should be
tried on sugarbeet wastes. Because of limited land availability at many
factory sites, the aerobic approach would not be applicable to all facto-
ries. It is recommended that further studies be conducted on anaerobic-
facultative ponds using coverings or controlled digestion with specific
organisms.
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SECTION HI
INTRODUCTION
The process of refining sugar from sugarbeets originated in Europe
following the first actual proof by Andreas Marggraf, a German chemist,
in 1747 (Z) that beet roots contained sugar. No use was made of this
discovery until 1799 when one of his pupils, Franz Karl Achard, re-
covered sugar from a small planting of sugarbeets. Napoleon himself
ordered the first large-scale planting of sugarbeets and the extraction
of sugar from the roots in 1811. Although some evidence exists that
the California Indians extracted sugar from beets prior to the Europe-
an development, the European continent is credited as the birthplace of
the beet sugar industry.
Following numerous unsuccessful efforts, the first generally accepted
commercial success to produce sugar from sugarbeets in the United
States is acknowledged to have been accomplished by E. H. Dyer at
Alvarado, California in 1879 (20).
The factory at Alvarado continued in operation through 1967 at which
time the Holly Sugar Corporation elected to terminate its operation and
dismantle the equipment. One of the significant influences on the de-
cision by Holly to terminate a near-century operation was the problem
and cost of waste disposal. The encroachment of the Bay area popula-
tion around the factory site created numerous problems in community-
industry relations. This historic beet sugar factory thus has yielded to
urbanization. This is a typical example of similar conditions existing
at other beet sugar factory sites and with other processing industries.
The technology of American industry has not yet advanced to the point
where factories are welcome to operate adjacent to residential and
business areas. Perhaps the day will come as processing techniques
become more sophisticated. Each present-day development in environ-
mental control is a building block in this direction.
The beet sugar industry is a typical American business enterprise. It
has its problems of air and water pollution. With the advent of increas-
ing public sentiment to clean our air and water, it behooves the sugar
industry to reduce its contribution to pollution as rapidly as technology
and economics permit.
The work here reported is essentially devoted to the problems of treat-
ing and disposing of wastes encountered in the water used to transport
-------
the beets in the factory and to wash the beets. Other sources of
waste such as process water, lime cake drainage, Steffen process waste,
condenser waste, etc. will be mentioned from time to time only to place
the entire discharge of wastes from a beet sugar factory into perspective.
Several sources have reported (20) that the total waste load from a
factory capable of processing 2, 000 tons of beets per day is roughly
equivalent to that from a city of 252, 000 people. Eldridge (8) reports
that 17.6 percent of the 5-day Biochemical Oxygen Demand (BOD5) dis-
charge from a factory will be in the flume water. However, this dis-
charge accounts for 72. 1 percent of the hydraulic volume. Excepted
from these figures is condenser water, a high volume, low BOD5 waste.
Recent reports by visitors returning from Europe have stated that con-
siderable success has been experienced in both water conservation and
waste treatment by applying recirculation or closed-loop systems to the
high volume water requirements of a factory. Particularly these reports
apply to the fluming and condenser waters. In the case of fluming water,
lime as CaO has been metered into the water to hasten precipitation of
settleable solids and to retard bacterial reproduction.
Several significant differences exist between European and North
American beet sugar processing campaigns. In the first place, European
campaigns are shorter than the average U.S. campaigns and are limited
to late fall and early winter. Secondly, nearly half of the U.S. beet sugar
production comes from sugarbeet roots that have been stored in large
open piles, whereas, only a small percentage of the European beets has
been subjected to short storage periods in small on-the-farm piles.
Thirdly, the climate in western Europe is quite uniform through the
entire processing season with small temperature changes. In contrast,
the North American sugarbeet processing campaigns are in progress, at
one location or another, 12 months ot the year.
European sugarbeet production and processing practices cannot be trans-
lated to North America without modification to correct for environmental
influences. The same is true within the North American continent.
Operational procedures in the southern part of California and southern
Arizona are quite different from those in North Dakota and Montana, and
the provinces of Canada.
Prior to initiating this study the influence of geographical location
was recognized. The proposed plan of operation included an analytical
program to guide the system operation and to predict the adaptability
of limed, recirculating (or closed loop) flume water systems to different
factory sites. It was agreed that a modified approach to several success-
-------
ful European systems of this type showed considerable promise for
adaptation in the North American continent. At the time of project plan-
ning some limited trials with limed, recirculating flume water were also
being planned by several U.S. and Canadian beet sugar companies.
Following several industry-wide conferences on the subject of flume
waste water treatment, the industry agreed to begin .a study of the prob-
lem through the Beet Sugar Development Foundation. An application for
supporting funds was submitted to the Environmental Protection Agency
(formerly the Federal "Water Quality Administration). The proposal
suggested the construction of a full-scale recirculating system at The
Great Western Sugar Company at Longmont, Colorado. Longmont is
within a geographical area which has climatic conditions relatively mean
to those existing within the states where processing plants are located.
The objectives were to develop a system for economic treatment of sugar.
beet factory flume (conveying and washing) water permitting its re-use
in a recirculating fluming system. The system should operate without
odor during and following the campaign. Any water surplus from the
system during operation, as well as the residual water after campaign,
was to be treated in a manner to meet discharge quality standards.
The plan of operation called for the addition of lime, caustics or other
chemicals to determine their effectiveness on control of pH, removal of
settleable solids and retention time. The precise treatment for the
surplus and residual water was not described since results of research
in progress were being awaited. Ultimately, the anaerobic approach
was selected by employing the principle of deep ponding and surface
aeration.
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SECTION IV
DESIGN AND CONSTRUCTION
The typical sugarbeet processing factory is designed to process either
freshly-harvested sugarbeets directly from farmers' fields delivered
by rail or truck or from large storage piles located at or near a facto-
ry. All sugarbeets are mechanically harvested by the farmer (or a con-
tractor) and delivered to receiving stations located on the factory pre-
mises and at convenient outlying sites. The receiving stations are
equipped with dry mechanical cleaning devices to separate the most
easily-removed dirt, clods, rocks, weeds and green leaf material from
the fresh roots. In some states the tare (removed material) is returned
to the individual farmer's field; in other states it must be retained at a
single location by the sugar company. Most of the additional adhering
dirt and extraeneous material is removed from the beets at the factory
by the fluming and washing operations.
Each beet sugar factory has an individual design for fluming and washing
operations. With few exceptions, each one will have a receiving hopper
or hoppers with flume water underflow. Some installations, particularly
for rail deliveries, will have high pressure overhead hoses that assist in
evacuating the cars. In cold climates, the water source to the overhead
sources is heated to thaw the frozen conglomerate of sugarbeets, mud,
dirt, rocks, etc.
From the receiving hoppers, the flume water transports beets through
a series of cleaning devices to remove sand, rocks, clods, organic
matter, metal, etc. A final high-pressure spray above the spray rollers
is the last cleaning operation prior to the slicing of the sugarbeets into
cossettes.
Historically, the flow design for fluming and washing provided for fresh
water input to the system and the discharge to holding ponds or to re-
ceiving water bodies. The design reported in this study provides for
the complete containment and recirculation of all fluming and wash
water.
The schematic flow diagram, Figure 1, will show an early and import
tant decision made in designing the flow pattern. The total flume and
wash water flow is not limed. Approximately one half is returned to
the flumes from the screens without being limed. The remainder of the
flow is limed, clarified and returned to the flume where it is mixed
-------
with the untreated flow. The proportion of treated to untreated flow be-
comes a part of the study.
In discussing the design and construction, only those system components
which are unique to the project will be given consideration. A discus-
sion of typical hydraulic components will be included only if they have
had particular influence on the operation and results.
FROM PLUMING OPERATIONS
TO NORMAL
•PLUMING OPERATIONS
HEATED WATER TO
SOAKING HOPPER
FIRST SETTLING
PONDS
OVERFLOW
FIGURE 1. SCHEMATIC FLOW DIAGRAM OF LONGMONT
FLUME SYSTEM.
The existing fluming system at the Longmont factory of The Great
Western Sugar Company between the receiving hoppers and the spray
rollers was only slightly modified. One major change was made at
the confluence of several waste streams before their discharge to the
old settling ponds. The design provided for the collection of the flume
water into a sump at which point it is pumped up into a manifold
supplying waste water to the elevated screens. Valves control the flow
to each screen (Figure 2).
10
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FIGURE 2. ELEVATED DSM SCREENS SHOWING MANIFOLD
AND VALVE SYSTEM.
FIGURE 3. PARSHALL FLUME AND HOSE ARRANGEMENT
FOR ADDITION OF MILK OF LIME.
11
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The final screen design included five stationary screens operating in
parallel. Four of the screens were Dorr-Oliver DSM screens. Three
had 3 mm openings and one screen had 6 mm openings between the stain-
less steel bars. The fifth screen was of similar design. However, it
had a longer and wider contact area with 6 mm openings. The rejects
from the screens drop to a trash platform and the underflow is collected
in a receiving manifold. The manifold divides the flow, about half of
which returns to the flumes. This flow is metered. The remainder of
the flow {that which is treated) is measured through a Parshall Flume
(at which point milk of lime is added, see Figure 3), passes through a
mixing box and is piped to the first settling ponds, only one of which
is used at a given time.
Considerable discussion preceded the decision to use the two-pond
design, rather than install a typical clarifier. Both plans would re-
quire a system for handling settled mud. The selected design requires
clamshell removal of settled mud from the alternately-used first ponds
during campaign. The selected design does not represent a preference,
but a means to reduce initial capital investment.
Figures 1 and 4 show the two semicircular first ponds lying outside the
perimeter of the central second settling pond. The flow can be directed
to either of the first ponds, the duration of flow to each being dictated
by the rate the settled mud accumulates and the percentage of settle-
able solids remaining in the first pond effluent. Since evacuation of mud
from, the ponds is accomplished by clamshell, wide dikes were planned
to permit ease of access.
Flow to the second settling pond from, either of the first ponds is by
gravity. In addition to the second pond serving as a second settling
pond, it serves as a surge basin. From the second pond, water is
pumped back to the flumes thus completing the cycle.
The anaerobic pond located to the side of the first and second ponds
serves as a reservoir. Water can be introduced into this pond through
a gravity syphon flowing from the second pond or can be pumped directly
to the pond from the recirculating system. Transport water is pumped
from the flumes and the first and second ponds at the end of campaign.
Conversely, anaerobic pond water can be pumped back to the recirculat-
ing system as make-up water.
12
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FIGURE 4. AERIAL PHOTO OF PROJECT SITE AND TREATMENT
PONDS.
The hydraulic design included provisions for emergency discharge.
Should the anaerobic pond be unable to contain the surplus waters,
water is wasted through a standpipe to a slough, and thence to the
river. Similarly, water can be wasted to the lime holding ponds
where the other miscellaneous factory wastes are retained.
13
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SECTION V
EXPERIMENTAL
General
It is important to mention that the experimental work described in this
report was superimposed upon the commercial processing schedule of the
Longmont factory of The Great Western Sugar Company. Ideal conditions
for experimental control were not always present. In recognition of the
typical events that transpire during a processing campaign, the design
was developed to minimize interference with the normal operation.
Under existing conditions, the variable quantity of sugarbeets delivered
to the flumes, the changing water flow rates, changes in water tempera-
tures and other variables were normal operational fluctuations. The
control and analytical schedules were designed to meet these variable
conditions as they developed. A fully-equipped mobile laboratory was
moved to a location on the factory premises conveniently near the samp-
ling points. The existing factory process control laboratory was inade-
quate to provide increased analytical activity.
The sampling and analytical schedule allowed for the measurement of all
flows wasted from the factory excluding domestic wastes. Although this
study was primarily conducted on the flume water, samples were routine-
ly collected from the condenser water sewer and on irregular schedule
from other waste streams. As unusual situations developed, supporting
bench and system studies were conducted. Reports of these are appended
as part of this report.
The experimental results reported cover the two operating campaigns of
19^7-68 and 1968-69. The principal emphasis has been placed on the
1968-69 data since some irregularities in the system's physical per-
formance during the first year influenced the validity of some of the re-
sults. Design modifications prior to the second campaign corrected near-
ly all of the hydraulic problems which had confounded the 1967-68 results.
15
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Sample CoIIetion
In most instances the samples for chemical analysis were taken at the
same location and at the same time as those for biological analysis.
The chemical samples and physical data were acquired and processed
at Longmont. The biological'samples were shipped immediately after
collection to the Department of Microbiology at Colorado State Universi-
ty in Fort Collins for processing. The data were evaluated by computer
at the Statistical Laboratory, Colorado State University.
In order to ascertain the fate of the chemical and biological constituents
in the system, five sites were selected as sampling stations (Figure 1).
The first pond influent (FPI) was designated as the initial sampling point.
The actual sampling point was located 6 feet distant from the discharge of
the pipe carrying water from the Parshall flume and lime mixing box
into the ponding area. Samples collected at this point contained the
mixed screened underflow and slurried lime.
The second point of sampling was located 6 feet distant from the dis-
charge of the overflow between the first and second ponds and was desig-
nated as the second pond influent (SPI). This site was selected to de-
termine the rate of which suspended solids would settle in the primary
pond and to determine the ratio of percent settleable solids removed to
detention time.
The third sampling point was at the outlet of the second pond at which
point the water was returned, by pumping, to the flumes. This site was
selected as the operations control point. At this location the total
change occurring across the ponds would be maximum. The differences
between the FPI and SPE reflected the removal efficiency of the pond
system and the SPE values established the amount of lime addition for
each selected pH parameter.
The fourth sampling points were located in the anaerobic pond. Two
representative locations were established on the pond centerline that
were equal distance from each other and the opposite two shorelines.
These points were each sampled at 3-foot vertical intervals. Initially,
an attempt was made to determine depth and location differences. Since
differences between depth intervals and location for both physical and
biological data were minimal, individual analyses were abandoned.
However, the sampling procedure was maintained to produce an anaerobic
pond depth composite (APDC).
16
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The fifth sampling point was at the anaerobic pond effluent (APE).
During the 1967-68 campaign there was a planned and continual dis-
charge from this point which required make-up water. During the
1968-69 campaign there was no discharge from the anaerobic pond,
thus no samples were taken; infrequent make-up water was re-
quired.
Automatic samplers were used at the first pond influent, second pond
influent and second pond effluent. The automatic samplers were used to
collect samples for chemical analysis only and were time-programmed
to collect a total of 2. 5 gallons during a 24-hour period at a rate of 12
sub-samples per hour. The sampling tubes were protected from
freezing with heat tapes. Standard grab methods were used for surface
and depth samples for dissolved oxygen, BOD5, and biological anal-
ysis (1).
The analytical schedule, analytical procedures and a description of
sampling methods used are shown in Tables 2.0 through 32 and in the
appendix.
Analytical Procedures
The numerous questions relating to the efficiency and operation of the
system were of hydraulic, mechanical, chemical and biological nature.
It became apparent that each of the stream flows associated withthe
system required quantitative evaluation. Each of the flows was meas-
ured with an appropriate metering device. Although the performance of
standard pumps, screens, valves, etc. were known, some questions con.
cerning durability under the design conditions were not answered until
placed under test.
The bulk of the analytical program involved the completion of the chem-
ical and biological analyses. Table 22 in the appendix gives a detail
of the routine schedule for the primary constituents believed to have an
influence on the system performance. Each of the analyses was rather
routine excepting that for total carbon. It had been reported that a
measure of the organic carbon in waste water might prove to be an
accurate substitute for measuring BOD5 loads in waste water (37).
A total organic carbon analyzer was used to obtain a value which was
then related to both BOD^ and COD measurements. Table 24 in the
appendix outlines the analytical schedule for biological analyses. Since
17
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234567 89 10 II
WEEKS
is ye
FIGURE 5.
RELATION OF DISSOLVED OXYGEN TO pH AT
THREE SAMPLING POINTS.
20
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The pH drop across the ponds increased as the FPI pH decreased from
pH 12.0 to 10.0. The largest pH reductions were experienced when the
FPI pH ranged from 8. 0 to 10. 0. When the FPI pH was from 7. 0 to 8.0,
it dropped at a slower rate and stabilized at the 6. 5-7. 0 level.
TABLE 2. --MEDIAN pH, FPI, SPE WEEKLY AVERAGE OF GRAB
SAMPLES THREE TIMES PER DAY.
FPI
pH
11.
11.
10.
9-
8.
7.
range
5-
0-
0-
0-
0-
8-
12.
11.
11.
10.
9.
8.
0
5
0
0
0
0
. Number
weeks
in
range
3
5
1
3
2
1
Median pH
FPI
11.
11.
10.
9-
8.
7.
8
1
1
4
4
4
SPI
11.
11.
10.
8.
7.
7.
6
0
1
8
8
0
SPE
11.
10.
9.
7.
6.
6.
4
6
4
6
8 •
8
As noted earlier, pH losses in the system were much greater in mag-
nitude and occurred faster when heated flume water was being used, re-
sulting in higher pond temperatures. In most cases, rising pond temper-
atures resulted in decreasing pH levels.
Higher lime addition (Figure 6, week 15) did not compensate for the in-
fluence of heated water on the rate of pH reduction.
Reference was made to a design decision providing for a portion of the
water to return from the screens to the flumes without treatment. The
percentage of the total flow returned to the flumes without lime addition
also correlates with pond pH (Figure 6). When the pond pH was below
10.0, the percentage of untreated return was less than 40 percent. When
the pond pH was above 10.0, the return percentage was greater than 40
percent. The ratio of lime addition to water was larger under these con-
ditions.
Although attempted, it was not possible from this study to separate the
effects of temperature and return flow percentage on pond pH. In gen-
eral, high temperatures and low return flow rates seem to be antago-
nistic to high pH control. Lime addition is most effective when return
flow is above the 40 percent level and the flume water is not being heated.
23
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Solids Removal
The suspended and settleable solids that were introduced into the fluming
and washing operations consisted of mud, sand, and beet fragments.
Some of the heavier solids were removed by the rock drag, which oper-
ates in the beet flume. The DSM screens removed an estimated 30 to
50 tons/day of wet material (Figure 7). Therefore, a large percentage
of the total suspended solids was removed before liming and before the
water entered the first settling pond. However, the water entering the
first settling pond, during the 1968-69 campaign, contained an average
56. 6 tons of suspended solids per day and the effluent from this pond con-
tained an average of 8.7 tons of suspended solids per day. Thus 47.9
tons of suspended solids settled in the first pond each day for an average
84.6 percent removal. By sedimentation tests it was determined that
94.8 percent of the settleable solids were removed. The fine solids
which did not settle readily continued to increase in the recycled waters.
Calculations based on settleable solids analyses showed that the average
mud deposition rate in the first pond was about 52,000 gallons (277 yd^)
per day. Since the Longmont factory sliced an average of 3, 307 tons of
beets per day, 15.7 gallons of first pond capacity was used for every ton
of beets sliced. Actual experience during the 1968-69 campaign, in-
volving the amount of time that was required to fill a first settling pond,
indicated that this figure is very nearly correct.
Based on the absolute density (Table 3) of the mud, the total weight of
the mud deposited and the total volume of the mud deposited, the average
percent moisture of the deposited mass was 80, 7 percent by weight.
This wet mud proved difficult to handle during campaign cleaning opera-
tions of the first ponds.
This settled mud was removed every three to four weeks during campaign
dependent upon the quantity of mud washed from "clean or muddy beets. "
Only about 85 percent of the mud could be removed from the ponds by
clamshell due to the high water content of the mud. After the end of
campaign, 100 percent mud removal could be accomplished.
Irregardless of the time of year when mud was removed, it was used
as landfill in low areas on the factory premises. This was necessary
due to the odors emanating from the mud, A lesser odor problem was
encountered from the mud removed from ponds after campaign.
24
-------
FIGURE 7. TRASH AND SOLIDS REMOVED BY SCREENING.
The moisture in the mud amounted to approximately 48, 000 gallons of
water per day. This water was lost to the fluming and ponding system
and amounted to 1. 4 percent of the total pond volume per day. The
water loss was, apparently, offset by an inherent increase in system
waters.
It was noted that the first pond would maintain a good settling efficiency
until it was almost full, at which time settleable solids would begin to
carry over into the second pond. The minimum retention time in the
first pond to achieve reasonable settling was determined to take between
20 to 30 minutes.
To further characterize the settleable solids in the first pond, the
settled mud in one liter of the 24-hour composite sample from the first
pond influent was removed daily and composited into weekly samples.
These samples were then analyzed (Table 3), The dry mud contained
an average of 3. 25 percent carbon (the average pH of the diluted sample
25
-------
TABLE 3.--WEEKLY MUD COMPOSITES,
AVERAGE.
1968-69 CAMPAIGN
Percent on
total solids
Average pounds
per day
Relative density*
wet, g/rnl
1.366
Absolute density** 2.59
g/ml
Total CaO
Soluble CaO
Alkalinity as CaO
Dissolved solids
Suspended solids
Total solids
Total carbon
6.36
1.25
0. 16
13.89
87. 11
100.0
3.25
6,230
1, 220
156
12,600
85, 200
97a 800
3, 200
*Relative density based on maximum compacted volume.
#*The calculated zero moisture density.
was 8.6). The carbon probably served as a substrate for bacteria and
thispH probably did not seriously inhibit bacteriological activity. Thus it
is easy to understand why the wet mud produced foul odors when it was
being removed from the first ponds.
The average amount of lime addition was 10, 440 pounds per day. The
amount of total CaO in the dry settled mud averaged 6, 220 pounds per
day. This means that as much as 59-6 percent of the lime added to the
system was lost immediately in the first pond.
The first pond was designed for primary settling of the heavy, more
readily settled solids. The second pond was designed to allow more
settling time and a milder environment to remove the smaller, more
difficult to settle solids. The average amount of solids entering the
second pond was 8. 7 tons per day. However, the amount of solids
leaving the second pond and returning to the fluming operations aver-
aged 9. 4 tons per day. This indicated that more insoluble solids were
26
-------
o °TOTAL SUGAR
o o ORGANIC ACID
o o pH 0
o
A
\ <* I
2 i . / '
* M / i
j \ A / '
i \ ' A\ / \
' o I / \ \ / °\
i ; \ I ' 1 V \
i ' \ I ! I ° 9 \
/ A°
^ i /
\!
I2.O
(1.0
10.0
9.0
8-0
7.0
U6.O
x
Q.
7,000-J
6.OOO-
5,000 -
4,OOO -
3,000 -
2,000 -
1,000
I 2 3 4 5 6 7 8 9 10 II 12 13 14 15 16
WEEKS
FIGURE 10. SPE RELATIONSHIPS BETWEEN TOTAL SUGARS,
ORGANIC ACIDS AND pH DURING CAMPAIGN.
The average concentration of total ortho phosphate in the second pond
during the 1968-69 campaign was 4.2 ppm= However, as only a trace
of phosphate is necessary to support an active biological population,
there was probably enough available phosphate in the system to support
biological activity.
Ammonia seemed to be the prevalent form of nitrogen as can be seen
from Table 5. Of the total nitrogen, 81 percent was ammonia nitrogen.
Ammonia nitrogen increased until the llth week of campaign reaching
a peak of 49ppm after which it steadily decreased. Nitrate and nitrite
nitrogen concentrations started above 7. 5 ppm and steadily decreased
until the 14th week when the concentration levels of these elements were
less than 0. 5 ppm, where they stayed for the remainder of the campaign.
31
-------
TABLE 5.--NITROGEN, SULFUR, AND PHOSPHOROUS CONCENT RA-
TIONS, 1968-69 CAMPAIGN.*
Range ppm Average
Maximum
PO4, total, ortho 9- 1
N03, nitrogen 12.0
NO^-nitrogen 8. 0
NH3 -nitrogen 50.0
Sulfate 853
Sulfite 9 . 6
Sulfide 2 . 0
Total inorganic nitrogen
Total sulfur
Minimum ppm
0.4 4.2
0.1 3.7
0.0 1.8
7.0 23.2
66.0 315
1.0 3.6
0.0 0.1
28.7
106
Average
pounds
in pond
99
87
42
546
7,410
84
2
676
2,510
^Combined results on both SPI and SPE.
Sulfate was the predominant sulfur compound in the recirculated flume
water. However, anaerobic and faculative bacteria systems can reduce
sulfate to the odor producing sulfide state (22). Note that the sulfide
concentration was as high as 2.0 ppm, but the average concentration of
sulfides was only 0. 1 ppm. Odor from the recirculating flume water
was noticeable at times but was never a problem during the 1968-69
campaign.
Anaerobic Pond
During the 1967-68 campaign the anaerobic pond was scheduled to receive
a 100 gpm flow from the second settling pond and to discharge a flow
equal to the influent minus the amount lost to seepage and evaporation.
The anaerobic pond was empty at the beginning of the 1967-68 campaign,
and during the early part of the season received the prescribed 100 gpm
32
-------
influent. However, the decision was reached to fill the anaerobic pond
rapidly in order to provide a supply of oxygen-demanding waste with
which to initiate anaerobic activity. The control by-pass valve was
opened to fill the pond rapidly, thus eliminating an opportunity to
accurately measure the influent flow.
Following filling, evidence of expected bio-degradation was absent.
About 2, 000 gallons of domestic sewage secondary sludge were added
to the anaerobic pond as inoculum to increase the digestion rate. The
results were quite negative; no activity was noted until the end of the
campaign.
Two five horsepower surface aerators (Aqua-Lator FLTM-5-4, Wells
Product Corporation) with complete anti-erosion assemblies were used in
the anaerobic pond. The purpose of the aerators was to spread a layer
of oxygenated water across the surface of the pond in order to oxidize
evolving, sulfides and other elements of the anaerobic digestion process,
thus reducing odors. Any reduction in oxygen demand accomplished by
these aerators was expected to be a fringe benefit as the pond was not de-
signed to be an aerobic facility.
During both campaigns the aerators worked reasonably well. Odors
from the pond were not excessive except during a period of high sulfide
liberation. This period lasted about 3 months. Near-zero weather did
not hamper aerator operation even though most of the pond surface was
ice-covered.
Some foam accumulated on the anaerobic pond from time to time, and
mounds of frozen foam piled around the aerators during the periods of
zero and sub-zero temperatures. A large build-up of foam was noted
at the Parshall flume during the 1967-68 periods of discharge.
Table 6 shows the range and mean of the analysis of the anaerobic pond
effluent during the 1967-68 campaign. The results of the anaerobic
pond experiences during the 1967-68 campaign suggested that the original
concept of an anaerobic pond as a campaign treatment facility would
need re-evaluation prior to the next period of operation. As a result,
the following decisions were made:
1. To eliminate the anaerobic pond effluent during campaigns so
as to hold all of the flume water in the pond system until
such a time as this water was sufficiently degraded and
acceptable for discharge to the river;
33
-------
2. To utilize the anaerobic pond as a holding basin which would
receive any excess water which might build-up in the settling
pond system;
3. To utilize the water residing in the anaerobic pond as a source
of make-up to the fluming and settling systems whenever needed.
The data will show that the 1967-68 post campaign water had been success
fully treated to meet discharge standards. Prior to the beginning of the
1968-69 campaign the anaerobic pond level was lowered to a water depth
of 8 feet. At this level the pond functioned as a reservoir to receive ex-
cess flume water with enough capacity to hold all of the expected excess
water. Additionally, a carry-over of active seed and sludge was desir-
able.
TABLE 6. --ANAEROBIC POND EFFLUENT, 1967-68 CAMPAIGN
PH
Total organic carbon
Filtered total organic
carbon
Total CaO
Ammonia nitrogen
Phosphate
5 -day biochemical
oxygen demand
Chemical oxygen
demand
Suspended solids
Volatile suspended
solids
Dissolved solids
Volatile dissolved
solids
Settleable solids
% by volume
Temperature °C
Flow gpm
High
7.4
460
429
511
17.0
0.4
1,190
1, 110
158
142
1,920
870
.03
6.0
171
Range""
Low
6.7
245
190
365
2.4
0.0
550
490
52
28
1,400
450
0.0
3.0
16
Mean
370
344
395
11.5
0.2
750
762
100
81
1,640
650
.01
4.0
86
Average
Ibs/day
discharge
383
356
409
11.9
0.2
777
780
104
84
1,700
670
*ppm unless otherwise noted.
34
-------
The anaerobic pond during the 1968-69 operating season successively
served as a surge reservoir for excess second pond water and as a
source of make-up water to the fluming system. No serious problems
were encountered. The flow pattern permitted an occasional feeding of
organic matter into the anaerobic pond. This was accomplished by
drawing water from the anaerobic pond into the flumes, which would
eventually cause the second settling pond to discharge into the anaerobic
pond. This recirculation procedure was employed several times in order
to increase the level of oxygen demanding substances in the anaerobic
pond for the purpose of maintaining continuing bioactivity.
As the 1968-69 campaign progressed the anaerobic pond temperature
steadily decreased. During the ninth week this temperature dropped
below 4°C and remained below for the rest of the campaign. The low
pond temperature (mean 6°C) probably inhibited biological activity as
little reduction in organics was measured during the 1968-69 campaign
(Table 7).
The pH of the anaerobic pond varied only slightly. It was highest before
any load had been added. When loaded the pH fell to about 7. 0-7. 5 and
changed only slightly after that (Table 9).
The total sugars were mostly degradated to organic acids by the time
the water reached the anaerobic pond. A small concentration of sugar
persisted, but it is believed that these are carbohydrate forms that are
difficult to degrade.
Some of the finer suspended solids carried through to the anaerobic
pond. Theoretically, this is good since the fine particles may provide
an inert nucleus for growth of biological floes (36). Sulfides were pro-
duced in the pond from time to time, but the average concentration was
only 0. 2 ppm. The almost negligible odor was also evidence of low
sulfide production.
TABLE 7. --ORGANIC DEGRADATION IN ANAEROBIC POND,
1968-69 CAMPAIGN.
BOD5
COD
Ib in pond
end campaign
minus begin
campaign
A
60,000
97,000
Ib
loaded
B
105,000
175,000
Ib
discharge
to flumes
C
43,000
65,000
Ib
degraded
(B-C) -A
5,000
13,000
35
-------
TABLE 8. --ANAEROBIC POND DURING CAMPAIGN, 1968-69
CAMPAIGN AVERAGE.
pH
Total sugar, sucrose
Suspended solids
Dissolved oxygen
Ammonia-nitrogen
Ortho phosphate
Nitrate -nitrogen
Nit rite -nit r ogen
Sulfate
Sulfite
Sulfide
High
8.4
160
421
9.2
33
2.7
2.5
0. 1
676
9.15
1. 1
ppm
Low
6.9
0
8
0
5
0
0
0
321
1.1
0
Mean
7.
62
156
1.
10.
0.
0.
0.
399
2.
0.
6
2
0
9
6
01
8
2
When the fluming operations ceased, the water in the first and second
ponds was discharged to the anaerobic pond for biodegradation after
both the 1967-68 and 1968-69 campaigns. The results from these two
years have not been combined, but were similar. The data from 1968-
69 are reported below in detail with occasional reference to 1967-68
treatment.
After the end of beet fluming in January 1969, the first and second
settling pond water was recirculated through an evaporator-condenser
(CSF) for one week prior to its discharge into the anaerobic pond.
This was done to increase the temperature of the fluming water before
its discharge into the cold environment of the anaerobic pond so as to
increase the bioactivity in the fluming water and thus accelerate the
rate of degradation. The settling pond temperature during this period
of recirculation was maintained at about 30°C. After the heating and
recirculation period the first and second settling pond water was pumped
to the anaerobic pond. The pond level had been kept low enough to re-
36
-------
ceive all of the water from the settling system so there was no resulting
discharge.
The water remained in the anaerobic pond until mid-September, 1969.
At that time the biological stabilization of the organics was nearly
complete and pond contents were subsequently used to fill the flumes
for the 1969-70 campaign.
The two 5-hp aerators ran continuously (except for short periods of
mechanical failure and planned experimental shut-downs) until the last
week of July, when a high concentration of algae was noted. The
aerators remained off until the last week in August, at which time
mechanical aeration was resumed.
Phosphate was added to the pond six times during the post-campaign
period to accelerate biological activity since the phosphate analysis in-
dicated a deficiency for optimum activity. The first two additions of
phosphate were in the form of triple super phosphate, a granular com-
mercial fertilizer containing 46 percent P2O$° However, the granular
material dissolved slowly and all subsequent additions were in the form
of ammonium phosphate, a liquid commercial fertilizer with a 10 per-
cent ammonia nitrogen and 34 percent P2O5 analysis. The liquid addition
proved to be satisfactory; adequate levels of soluble ortho phosphate
were achieved.
After the campaign of 1968-69, the anaerobic pond was sampled in the
same manner as during the 1967-68 post-campaign period, except that
the samples were composited by depth in an attempt to explore the pos-
sibility of stratification. This sampling procedure was continued for
the first 8 weeks of the post-campaign period. From the data it was
determined that stratification did not exist in the pond and that extensive
sampling was not necessary for depth differences. Table 30 in the
appendix shows the analytical schedule which was conducted on the
anaerobic pond samples for the first 8 weeks of the post-campaign peri-
od (February 3 to March 28, 1969).
Beginning with the 9th week of the post-campaign period, the anaerobic
pond was sampled as described above. However, all samples were
composited. Table 3 1 in the appendix shows the analytical schedule
performed until July 9, 1969, and Table 32 shows the analytical
schedule continued thereafter.
On February 5, 1969, the anaerobic pond was at a depth of 11' 4" and
contained more than 145, 000 pounds of BOD5> Under conditions of high
37
-------
TABLE 9.--ANAEROBIC POND; POST CAMPAIGN 1967-68, 1968-69;
BOD5 REDUCTIONS.
Temperature range C°
Phosphate added* - Ibs.
BOD5 reduced, average Ibs/day
Post
campaign
1967-68
1/23 to
4/16/69
3-10
0
321
Post
campaign
1968-69
2/3 to
4/30/69
3 - 12
68
388
Post
campaign
1968-69
5/7 to
7/30/69
15 - 25
998
1, 145
^Soluble ortho phosphate
The BOD,- curve was similar to the organic acid curve, (although the
cycles showed a different frequency) as the areas under both curves
differed by less than 2 percent (calculated from the first to the 24th
week). This indicated that most of the BODc in the system could pos-
sibly be attributable to organic acids. The COD curve was more con-
stant and not subject to many concentration variations.
The decrease in dissolved solids seemed to follow the COD curve until
the 17th week when the two began to diverge. At that point the rate at
which dissolved solids were removed became much less than the rate of
COD removal. At the 31st week a concentration of nearly 2, 700 ppm of
dissolved solids remained, probably as mineral salt forms.
Sulfates diminished in the system until the 12th week when they reached
a very low level. It is assumed that the facultative and anaerobic organ-
isms utilized sulfate in the production of odor-producing sulfides. The
sulfide curve relates inversely with the sulfate curve as the concentra-
tion of sulfides increased until the sulfate concentration was at a minimum.
The sulfides then dissipated until the 20th week when they disappeared.
Odor produced by the sulfides was very distinct during much of the 1968-
69 post-campaign period even though the aerators were operating con-
tinuously.
Total and soluble CaO continued to be reduced in the anaerobic pond.
Their reduction might be explained by the precipitation of insoluble
calcium compounds. During the 31-week period more than 56, 700
pounds of total CaO was removed of which more than 41, 900 pounds was
soluble (Table 11). As would be expected from the calcium data, total
acids also were reduced by more than 61S 500 pounds. Soluble CaO
41
-------
accounted for 68. 2 percent of the total acid reduction.
Ammonia was the prevalent form of nitrogen in the pond as high valence
nitrogen concentrations never exceeded 0.5 ppm (Figures 12 and 13).
This could be expected as facultative and anaerobic systems reduce
high valence compounds to a low valence state. Ammonia concentra-
tions showed no regular trends as both large increases as well as de-
creases were noted. It is theorized that the decreases are due to the
utilization of ammonia by the bacteria and algae as a source of nitrogen,
and that the increases are due to the nutrient addition as well as the
breakdown of nitrogen-containing organic compounds (and the subsequent
release of nitrogen to the pond waters).
Dissolved oxygen was absent until the 28th week, at which time a trace
of D.O. was noted (Figure 13). About 3 weeks earlier the pond had de-
veloped a definite green color. Biological analyses revealed the pres-
ence of green algae, but many of the algae masses were "cut up, "
presumably due to the aerators. The aerators were shut off during the
26th week and D. O. was noted 2 weeks later. However, 4 weeks later
the D. O. level in the pond had not increased as expected and the BOD5
and COD reduction rates had slowed considerably. At the beginning
of the 30th week, both aerators were turned on, resulting in a quick rise
to 4.0 ppm D.O. and increased rates of BOD and COD reductions. The
water reached discharge quality one week later (Figures 12 and 13).
These experiences indicate that mechanical aeration is helpful to the
final polishing in deep pond treatment of sugarbeet wastes due both to
oxygen addition and mixing.
As previously stated, phosphate addition appears necessary as evidenced
by its utilization in the biologically active pond (Figure 12). However,
there is further evidence of phosphate release since high levels of phos-
phate were noted that exceed the amount artificially supplied. The
phosphate level in the pond did not decrease significantly after the 25th
week (Figure 12, week 25). It is probable that phosphate was continual-
ly released, but during periods of high biological activity, it was imme-
diately utilized and therefore, did not appear in the phosphate analysis.
This was also observed in the 1967-68 data where no phosphate was
added. However,, as the biological activity decreased (due to the ab-
sence of degradable materials) so did the rate of phosphate utilization;
the phosphate level remained constant.
It is concluded that the addition of phosphate is necessary to produce
a highly-active biological system. The natural phosphate release
mechanism appears to proceed too slowly to supply needs. The dis-
42
-------
25. Nesbitt, J. B. 1969. Phosphorus removal - the state of the art.
J. Water Pollution Control Fed. Part 1:701-713.
26. Noller, C. R. 1951. Textbook of organic chemistry. 2nd ed.
W. B. Saunders & Co., Philadelphia, Pa. and London, England.
27. Norman, Lloyd W., James E. Laughlin and L. O. Mills. 1965.
Wastewater treatment studies at Tracy, California. J. Am, Soc.
Sugar Beet Technol. 13(5):415.
28. Parker, C. D. and G. P. Skerry. 1968. Function of solids in
anaerobic Lagoon treatment of wastewater. J. Water Pollution
Control Fed. Parti pp. 192-204.
29. Riehl, M.L., H. H. WeiserandB. T. Rheins. 1952. Effect of
lime treated water upon survival of bacteria. J. Am. Water Works
Assn. 44:466-470.
30. Rose, R. E. and W. Litsky. 1965. Enrichment procedure for use
with the membrane filter for the isolation and enumeration of fecal
streptococci in water. Appl. Microbiol. 13: 106-108.
31. Schaffer, R. B., C. E. Van Hall, G. N. McDermott, D. Earth,
V. A. Stenger, S. J. Sebesta and S. H. Griggs. 1965. Applica-
tion of a carbon analyzer in waste treatment. J. Fed. Water
Pollution Control Fed. February 1967. pp. 1545, 1560.
32. Snedecor, G. W. 1946.
State College Press.
Statistical methods. 4th ed. Iowa
33. Spreece, R.E. and P.L. McCarth. 1962. Nutrient requirements
and biological solids accumulation in anaerobic digestion. Pergamon
Press, Oxford, London, New York and Paris.
34. U.S. Department of Agriculture. 1969- Sugar statistics and re-
lated data. Statistical Bulletin No. 244. Volume II (Revised).
Washington, D. C.
35. U.S. Department of Interior. Fed. Water Pollution Control Adm.
South Platte River Basin Project. 1967. The beet sugar industry -
the water pollution problem and the status of waste abatement and
t r e at ment. p. 144.
49
-------
36. Walters, C. F., R. S. Engelbrect and R. E. Spreece. 1948.
Microbiol. substrate storage in activated sludge. J. Sanitary Eng.
Div. Proceedings Am. Soc. Civil Eng. 94 (SA2).
37. Williams, R. T. and R. A. Taft. 1966. The carbonaceous analyzer
as water pollution research tool. Instrument Society of America.
Reprint No. 5.2-4-66.
38. Personal Communication, Amalgated Sugar Company.
50
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TABLE 14 (continued)
First Second
pond pond
C orrelation influent influent
7.
pH and
Total carbon -.698 -.433
Alkalinity .752 .792
Second
pond
effluent
-.410
.797
Total carbon and
Total acids
. 151
-.403
-.301
Date and
Total solids . 846
Suspended solids . 530
Dissolved solids . 896
Settleable solids . 548
910
645
888
377
924
693
910
363
10. Total solids and
Suspended solids . 834
Dissolved solids .917
646
993
689
992
11. Suspended solids and
Dissolved solids . 545
Settleable solids .913
553
779
596
845
12. Dissolved slids and
settleable solids
.552
411
258
13. Recirculation rate and
Control pH .602
Lime addition -.475
Volatile solids correlated well with the total solids during 1968-69 and
with BOD, COD, and TOC. This is due to the carbonaceous nature of
a large percentage of the volatile solids.
Tables 15 and 16 relate to the anaerobic pond during campaign. During
the 1967-68 campaign the anaerobic pond produced very few valid correla-
tions, but during the 1968-69 campaign many significant correlations were
obtained. It is interesting to note that most of the correlations established
57
-------
TABLE 15. --CORRELATION COEFFICIENTS; ANAEROBIC POND DURING CAMPAIGN;
LONGMONT FACTORY; 1968-69.
PH
BOD5
COD
Sol. CaO
Tot. CaO
Tot Sug
TS
SS
S DS
TS
Org Acids
Temp
Tot carbon
Dissolved O?
Ammonia
nitrogen
Date pH
-.55
-.92 -.53
.91 -.57
.88 -.44
.92
-.47
.93 -.53
,48
.95 -.48
.91
.91
-.55
.94
-.70 .75
BODc;
.94
. 90
.89
.95
.71
. 94
.86
.88
-. 82
.94
.63 -
.55
Sol. Tot Tot Tot Org
COD Cao CaO Sug TS SS DS Acids Acids Temp
.92
.89 .94
.98 . .91
.70 .66 .57 .72
.97 .92 .92 .99 .62
.91 .89 .87 .92 .55 .94
.92 .88 .88 .92 .50 .94 .90
-.75
..96 .97 .94 .56 .98 .76 .97 .89 .86 - . 97
.73 .76 -.64 -.69 -.73 -.55 -.86
.67 .56 .52 .67 .82 .58 ,43 .49
-------
TABLE 16. CORRELATION COEFFICIENTS FROM ANAEROBIC
POND; 1967-68 CAMPAIGN.
Filt.
TS TVS SS DS TOC COD
TVS
DS
VDS
VSS
TOC
.97
.99 .95
,96 .98 .97
.95
.72 ,71
in the first and second ponds carried through to the anaerobic pond where
a semi-stagnant concentration of organic acids correlated with BOD5.
However, a valid BOD$ to organic acid ratio was not established in the
settling pond system. This is possibly due to settling of the insoluble
organic acid salts in the static environment of the anaerobic pond and
incomplete settling of these salts in the turbulant environment of the re-
circulated water.
Biological Analysis
During campaign, grab samples were taken of the second pond influent,
second pond effluent and anaerobic pond and analyzed biologically. The
data show that both coliform and fecal streptococci increased as campaign
progressed at both the secondary pond influent and effluent (Table 17). and
Table 18).
This was probably due to a constant input of these organisms from beet
washing and from recycling of second pond water. This would offset
death of the organisms that could be expected from the lime treatment.
The total aerobic and anaerobic counts also increased but slower than the
indicator organisms as campaign progressed. This would be due to one
of several factors: death of the organisms and precipitation in the lime-
treated primary system are removing more of these general microbial
forms; also many of these organisms could be forming clumps which do
not give a true plate count in the laboratory.
59
-------
The increase for both the total counts and the indicator organisms are
greater at the influent than at the effluent. This would indicate that
some of these organisms are being removed in the second pond. The
removal of total anaerobic bacteria and coliform are more effective than
the removal of total aerobic bacteria and fecal streptococci.
At the second pond influent the very high negative correlation seen bet-
ween the date line and NO3-NO2 nitrogen (Table 17) indicates that even
in the short exposure time of the primary system, microbial breakdown
of these nitrogenous substrates is initiated. This is supported by the
slight increase in NO^-N seen as time .progressed.
With only five observations at the second pond influent streptococci and
coliforms correlated at 78 percent. Coliforms and total aerobic and
anaerobic counts only correlated at about 60 and 54 percent, respective-
ly, while fecal streptococci and total counts correlated at 72 and 71 per-
cent with 17 observations. As waste load increased, as shown by COD
and BOD readings, the coliform counts increased with a fair correla-
tion. Similar correlation between streptococci and COD and BOD occur-
red. (Poorer (50-60 percent) correlation between total aerobic and
anaerobic counts and waste was observed.)
The coliform correlations seem to be due to the direct relationship of
the organisms to total acids and organic acids which were increased
and to NO3-NO2N which decreased; but not related to NH3-N. Simi-
larly, total organic carbon rose parallel to the coliforms. Also, fecal
streptococci correlated in a similar manner with total acids and organic
acids and with decreasing NO3-NO2^. Excellent correlation to TOC
was seen. The total aerobic bacteria correlations to these same factors
were poor, as were the anaerobic count correlations. This is due to the
very diverse metabolic activities of these organisms. It should be noted
that the correlation between total aerobic and anaerobic bacteria is ex-
cellent, probably due to the fact that in both groups we are really chief-
ly measuring the number of facultative organisms.
The BOD and COD levels correlate almost perfectly, and with the indica-
tion that BOD correlates with total acids, organic acids, NO3 and NO^N
and even with ammonia-N, there is evidence the waste load is almost
exclusively organic material rather than inorganic salts. This is also
seen in the TOC vs. BOD correlation and also with the COD correlations
with the same factors.
In the observations of each organisms group counted there is further evi-
dence that counts drop as pH rises. Only the streptococci seem to show
60
-------
a correlation of significance (77 percent).
The pH vs. TOC correlation of -74 percent further emphasizes the crit-
ical nature of the pH of the system for the control of micro-organisms
by increasing pH.
Coliforms and fecal streptococci rose in a parallel manner but again did
not correlate as well with the total counts. The aerobic and anaerobic
total counts rose with a good degree of correlation, again pointing to
the facultative nature of the system. The coliforms increased similarly
as the BOD and TOC while the streptococci correlated to a lesser de-
gree, and total aerobic and anaerobic bacteria correlated poorly. The
coliforms agree well with total acids but to a marginal degree with organ-
ic acids. Fecal streptococci seem to be better related to these acid
measurements, but total counts seem completely unrelated even though
they are present in far greater numbers than the indicator organisms.
Coliforms do relate well with total organic carbon and less with
NO-j-N. Both coliforms and fecal streptococci show the expected drop
as pH rises, but the total counts show no relationship to pH.
In the second pond no other discernable biological relations are detect-
able. This probably is due to the temperature, pH and short retention
time. Some biological activity is evident; however, this portion of the
system seems to be an acclimatization zone for the organisms. Also,
the recycling of water back to the flumes has a continuing input of new
materials, both biological and chemical. V^
In the anaerobic pond, relatively few coliforms were found, and the num-
bers did not vary greatly during campaign--ranging from about 10 to
1, 000/ml in 1968-69 and less than 100 in 1967-68. Fecal streptococci
were about 10 times as numerous as coliforms and did increase as the
campaign progressed. Again, this indicates the greater survival power
that fecal streptococci have over coliform. Aerobic and anaerobic
counts were quite a bit more numerous, as expected, but did not vary
in relation to time with any correlation. Mean numbers were over
10° organisms/ml.
As at the other sampling points, COD and BOD correlated with time and
with each other (Table 19). As in the primary-secondary pond system,
there is good indication that the BOD as well as COD consists of bio-
degradable materials. In this biologically active unit, ammonia-N
does correlate fairly well with time while the NO3-NO2N scatters ran-
domly. Also, the TOC-date correlation is almost perfect, indicating
61
-------
TABLE 17. CORRELATION COEFFICIENTS; SECOND POND INFLUENT SAMPLES TAKEN
FOR BIOLOGICAL AND CHEMICAL ANALYSIS; 1968-69 CAMPAIGN
M
Coliform
Fecal strep
Total
aerobic
Total
anaerobic
pH
BOD5
COD
Phosphate
Tot. acids
Organic
acids
N03+N02-N
N02-N
NHo -N
Suit it e
Sulfide
Tot. carbon
Tot. sugar
0)
•4-J
0)
Q
.83
-.68
.93
.85
.86
-.91
-.87
.79
-.86
-.98
a
FH
O
<-w
•F-l
1— t
O
U
,78
.60
.54
-.54
.82
.75
. 80
.85
-.79
.87
-.49
o
u £
• r-l O
$ fr *tt O "rt 0
^2 •£ ^ -ti ni
4> £ ° 0) O fl
M4 w H nJ H nj
.72
.71 -.60 -.65
-.78 -.60
.80
.66
.75
.81
-.76
-.66
.86 .62
.91
- . 43 -.35
E
OH
-.68
-.62
-.65
-.63
-.59
-.66
-.74
IT)
Q
O
cq
.88
.91
.91
-.89
-.89
.69
.72
.97
13
A ^H
S s *
O ^ o
U OH H
.91
.86 .97
-.84 -.88
-.76 -.86
.69
.63
-.71 -.73
.81
-.76
^
• iH - \-r \-3
a z I^H f-
w J3 w + 1 ' '
^ W) ^ ro ^ r*
• i^ . nH _» /^ IT
CJ h y O O 3-
rtj O nj IS 2 2
,
-.85
-.74 .96
.69-. 55 -.65
.72 -.64 .57
-.65 .96 -.56
.94-. 94-. 91
-.73 .68
; <^ a) CD
™ S 3
? S 15 3
< d d ^
•^ S
W (0 ^
.65 .84 .83
-------
TABLE 18.--CORRELATION COEFFICIENTS: SECOND POND EFFLUENT SAMPLES TAKEN
FOR BIOLOGICAL AND CHEMICAL ANALYSIS;1968-69 CAMPAIGN.
Coliforrn
Fecal strep
Total
aerobic
Total
anaerobic
PH
BOD5
COD
Phosphate
Total acids
Organic
acids
NO3+NO2-N
NO2~N
NH3-N
Sulfate
Sulfite
Sulfide
Tot. carbon
Tot. sugar
0)
rt
Q
.83
.80
-.67
.91
.88
.87
.81
-.89
-. 87
.83
.91
Coliforrn
.84
.75
.62
-.80
.76
.74
.80
.67
-.76
-.71
.67
.90
.86
-.70
o
£
-M o
*~1 n. •—",£* *-* *•"
™ S
J3 M + 1 ' ! td ** ""* R
bJO"3 fO (MrOMH^H jj 'S
1-1 "1 O Offi rt *rt Ofrt
Ort^ ££wwtHO
-.83
-.79 .93
.70 -.48 -.60
.69 -.71 -.68
.67 -.56-. 91 .66 .66
.97 -.85-. 80 .78
-.67 .67 -.79
-------
TABLE 19. --CORRELATION COEFFICIENTS; ANAEROBIC POND SAMPLES TAKEN FOR
BIOLOGICAL AND CHEMICAL ANALYSIS; 1968-69 CAMPAIGN.
6 y £ | 0 g
<1) ^3 "j 4) nj O n) CD Q Q ® ^ r£j g* r{§ ~H JM ro 43 iH
tti o
-------
the degradability of the waste and the low concentrations of COD-pro-
ducing salts of minerals.
A 5-6° decrease in water temperature during campaign had little effect
on the biological action.
While coliforms did not correlate with any of the physical and chemical
variables, the fecal streptococci did show 70-80 percent correlation
with BOD, COD, TOC organic acids, PO4 and total acids, but not against
the nitrogenous materials. It seems that in this pond, as observed
previously also, fecal streptococcus is a better index than coliforms if
one of the standard pollution indices must be used.
Total aerobic and anaerobic counts correlate very well with each other
but with no other parameter except pH and, to some degree, with temper-
ature. Again, we are measuring facultative types of cells.
Phosphate analyses showed low levels in the pond (mean less than 1 mg/
liter) with considerable scatter of results. As expected, as the organic
and total acids and TOC levels rose, the PO4 rose also but never to
levels over 1. 1 mg/liter. This may indicate the limiting effect of the
lack of PO^ on microbial activity allowing build-up of wastes. In this
waste the organic acids and total acids seem to be the same and also
about the same materials as measured to TOC.
65
-------
-------
APPENDIX II
TABLES
No. Page
20. Abbreviations Used in this Report, Alphabetical Order 69
21. Description of Analytical Procedures 70
22. Analytical Schedule, FPI, SPI, SPE for each Week of
Campaign, 1968-69 76
23. Analytical Schedule for each Week of Campaign 1967-68 77
24. Analytical Schedule for Samples for Biological Analysis,
SPI, SPE, APDC for each Week of Campaign 1968-69 78
25. Analytical Schedule, First Pond Mud Samples, 1968-69 78
26. Physical Data Schedule, 1968-69 Campaign 79
27. Analytical Schedule, Condenser Water and Miscellaneous
Factory Effluents impounded for each Week of Cam-
paign 1968-69 80
28. Analytical Schedule, Anaerobic Pond Samples, 1967-68
Post Campaign, February 3 to March 28, 1968; Three
Samples per Week 81
29- Analytical Schedule (twice weekly), Anaerobic Pond,
1968-69 Post Campaign, February 3 to March 28, 1969 81
30. Analytical Schedule, Anaerobic Pond Samples; 1968-69
Post Campaign, April 2 to July 9, 1969, One Sample
per Week 82
31. Analytical Schedule (weekly), Anaerobic Pond Samples,
1968-69 Post Campaign, July 17 to September 3, 1969 82
67
-------
TABLES (continued)
No.
32.
Analyzed Substances Entering and Leaving the First
and Second Ponds in Series, Showing Percentage
Removed by the Ponds per Ton of Beets Sliced,
1968-69 Campaign Average 83
33. Primary Pond Influent, 1967-68 Campaign, Composite
Sample Analysis for BOD, COD, TOG, Filtered TOG,
Organic Acids, Total CaO, Soluble CaO, Alkalinity, pH 84
34. Dilution Effect on pH in Primary Pond of Fresh Make-
up Water Added to System, 1967-68 Campaign 85
68
..
-------
TABLE 20.--ABBREVIATIONS USED IN THIS REPORT, ALPHA-
BETICAL ORDER.
1. Alk.
2. APE
3. APDC
4. APG
5. BOD5
6. COD
7. CWE
8. DO
9. DS
10. EHPI
11. Filt. TOC
U. FPI
13. gpm
14. MPN
15. NH3-N
16. NO3-N
17. NO2-N
18. Org. Acids; OA
19= PO4
20. PPC
21. PPE
22. SO4
23. SO3
24. Sol. CaO
25. SPE
26. SPI
27. SS
28. S
29. Sue.
30. T°C
31. TOC
32. Tot. Acids
33, Tot. CaO
34. Tot. Sug.
35. TS
36. TVS
37. VDS
38. Vol.
39. VSS
Alkalinity
Anaerobic Pond Effluent
Anaerobic Pond Depth Composite
Anaerobic Pond Grab
Biochemical Oxygen Demand (5-day)
Chemical Oxygen Demand
Condensed Water Effluent
Dissolved Oxygen
Dissolved Solids
East Holding Pond Influent
Filtered Total Organic Carbon
Filtered Pond Influent
Gallons per minute
Most Probable Number
Ammonia Nitrogen
Nitrate Nitrogen
Nitrite Nitrogen
Organic Acids
Soluble Phosphate
Primary Pond Center
Primary Pond Effluent (Secondary Pond Influent)
Sulfate
Sulfite
Soluble CaO
Second Pond Effluent (Anaerobic Pond Influent)
Secondary Pond Influent
Suspended Solids
Sulfide
Sucrose
Temperature Degree in Centigrade
Total Organic Carbon
Total acids/meq. /liter
Total CaO
Total Sugars
Total Solids
Total Volatile Solids
Volatile Dissolved Solids
Volume
Volatile Suspended Solids
69
-------
TABLE 21. --DESCRIPTION OF ANALYTICAL PROCEDURES.
Analysis
Description
1. Total sugars
anthrone method
2. Total CaO
3. Soluble CaO
4. Biochemical
oxygen demand
5. Chemical oxygen
demand
6. pH
This determination involves mixing 5 ml
anthrone H^SO4 solution with 1 ml of filtered
sample and heating in a boiling water bath
for 10 minutes. A color is developed which
is proportional to the amount of sugar pres-
ent. The absorbancy of this color is read on
a colorimeter, and by comparison with the
graph of the absorbancy standard, sucrose
can be determined.
The method employed for this determination
involves mixing a measured volume of sample
with enough concentrated HC1 to dissolve all
of the insoluble calcium and diluting to a
known volume. An alequot is then titrated
with standard versenate solution to the
Univer I end point.
In this determination a sample was filtered,
and an alequot was titrated to the Univer I
end point with standard versenate solution.
The procedure described in "Standard
Methods for the Treatment of Water and
Waste Water, " 12th edition, was utilized.
The procedure utilized in this determination
is described in "Standard Methods of the
Treatment of Water and Waste Water, " 12th
edition, except that the end product was read
colorimetrically in a Hach DR Colorimeter,
Model 1104, rather than titrated. During
1968-69 the results were determined by titra-
tion.
pHs were read directly on a Leeds and
Northrup pH meter.
70
-------
TABLE 21. --(continued)
7.
Total organic
carbon
Filtered total
carbon
Total acids
10= Ammonia
nitrogen
11. Phosphate
A total organic carbon analyzer manufactured
by the Laboratory Equipment Corporation
(LECO) was used for the determinations of
organic carbon. No attempt was made to
correct results for errors due to CO2 and
CO3.
The insoluble matter was separated from the
solution by means of filtration. A sample of
the solution was then analyzed with the "LECO"
carbon analyzer. CO? was not removed prior
to analysis.
A measured sample was put through a column
containing Dowex D-50 ion exchange resin.
This resin is the strong cation type which ex-
changes H+ ions for positively charged ions in
the solution. The effluent from this column
was then titrated with a standard solution of
sodium hydroxide to the phenolphthalein end
point.
The direct Nesslerization procedure as de-
scribed in "Standard Methods for the Treat-
ment of Water and Waste Water, " 12th edi-
tion, was employed in this determination.
The end results were obtained by a Hach DR
Colorimeter, during the 1967-68 campaign.
But during the 1968-69 campaign results were
obtained by use of a Spectronic 20 (a Bausch &
Lomb colorimeter-spectrometer) utilizing a
standard calibration curve.
Phosphates were determined, during the
1967-68 sugar year, by utilizing the stannous
chloride reduction in an ammonium molybdate
solution. Final results were obtained by the
use of a Hach DR Colorimeter. A more com-
plete description of this method may be found
in the Hach DR Colorimeter manual for use
with the Model 1104 Colorimeter. During the
71
-------
TABLE 21. --(continued)
Analysis
Description
12. Alkalinity
13. Solids
1968-69 campaign ortho phosphate was deter-
mined by the method described in "Standard
Methods for the Examination of Water and
Waste Water, " 12th edition, pp. 234-236.
A measured volume of sample was titrated
against a standard acid or base solution to
phenolphthalein end point.
Solids analyses included total solids, total
volatile solids, suspended solids, volatile
suspended solids and settleable solids.
Settleable solids were analyzed by means of
an Imhoff cone; the other solids were analyzed
by the procedure outlined in "Standard Methods
for the Treatment of Water and Waste Water, "
12th edition.
14.
Dissolved
oxygen
15. NO3 + NO2-N
16. Organic
acids
Dissolved oxygen was analyzed according to
the procedure described in "Standard Methods
for the Treatment of Water and Waste Water, "
12th edition; the azide modification of the
Idometric method was used.
Analysis for NO^ and NC>2 nitrogen were com-
pleted by adding Hach Nitraver + Nitriver pow-
der pillows to samples and standard NC>3+NC>2
solutions. The final results were determined
colorimetrically on a Spectronic 20, Bausch
& Lomb Colorimeter.
Organic acids were determined according to
the procedure described in "Water and Waste
Water Analysis Procedures, " Volatile Acids
section, p. 72. This manual was published
August, 1967 by Hach Chemical Co. Final re-
sults were obtained colometrically utilizing a
Spectronic 20 colorimeter and Standard Acetic
Acid calibration curve.
72
-------
TABLE 21. --(continued)
Analysis
Description
17. Sulfates (SO4)
18. Sulfites (SO3)
19. Sulfide
20. Coliforms
Sulfate analyses were completed utilizing the
gravimetric procedure described in "Standard
Methods for the Examination of Water and
Waste Water," IZth edition, pp. 287-290.
Analyses for sulfite were completed utilizing
the procedure described in "Standard Methods
for the examination of Water and Waste Water, "
12th edition, pp. 294-296.
During the 1967-68 campaign sulfide analyses
were completed by the method described in
"Standard Methods for the Examination of
Water and Waste Water, " 12th edition, pp. 427
&428. After the 1968-69 campaign sulfides
analyses were completed utilizing a "La Motle-
Pomeroy" Sulfide test kit.
(APHA, Standard Methods, 12 ed., 1965).
Appropriate aliquots of sample were placed in
a Hydrosol filter funnel (Milipore) containing a
47mm type HA (pore size 0. 45 u) white mem-
brane filter (Milipore). In cases where the
sample aliquot was less than 10 ml, there was
a sterile buffered water carrier placed in the
funnel to assure even distribution of the organ-
isms on the surface of the membrane. Using
a vacuum system, the sample aliquot was drawn
through the membrane and the sides of the
funnel were washed with 25-50 ml of buffered
sterile water.
The membrane was then placed in a petri dish
(60 x 16 mm) containing an absorbent pad with
2.0 ml of m-Endo Broth MD (Difco) medium.
The petri dish was placed in a moist chamber to
prevent drying and incubated at 35°C for 18-24
hours at which time the plates were counted
using a stereo disecting microscope with obique
73
-------
TABLE 21.--(continued)
Analysis
Description
21.
Fecal
streptococci
22.
Total aerobic
count
lighting. Typical colonies were dark with a
gold-green metallic sheen.
(Difco Laboratories; Detroit, Michigan)
(Millipore Corporation; Bedford Massachu-
setts)
Aliquots of sample were filtered through a
membrane filter as per coliform determina-
tion.
Enrichment: (Rose and Litsky, 1965). In the
lid of a petri plate with solidified m-Entero-
coccus Agar (Difco) in the bottom, an absorb-
ent pad was placed with 2. 0 ml of m-PYC
(Difco) medium. The membrane was placed
in a moist chamber and incubated at 35°C for
3-6 hours.
Transfer and differential medium: (APHA,
Standard Methods, 1965). At the end of the
3-6 hour enrichment, transfer the member to
the surface of the m-Enterococcus Agar (Difco)
in the bottom of the petri dish and continue in-
cubating at 35oC for an additional 48 hours.
All red and pink colonies were counted using a
stereo dissecting microscope with oblique
lighting.
(Millipore, 1969). Sample aliquots were fil-
tered as per coliform test, but black membrane
filters were used. The membranes were
placed on an absorbent pad with 2. 0 ml of m-
Plate Count Broth (Difco) in a sterile petri
plate and incubated in a moist chamber at 30°C
for 48 hours. All colonies (0-300) were
counted using a stereo dissecting microscope
with oblique lighting. The black membrane elim-
inated the need for contrast staining to make all
colonies easily distinguishable.
74
-------
TABLE Zl.--(continued)
Analysis
Description
23. Total anaerobic
count
(Millipore, 1969) (Harris and Coleman, 1963).
Sample aliquots were filtered through mem-
branes as in the coliform determination; again
the black membranes were used. The mem-
brane was placed directly on the surface of sol-
id Plate Count Broth (Difco) in a petri dish.
This dish was placed in a dessicator jar which
was evacuated and flushed with nitrogen three
times. Finally with a slight vacuum remaining
in the dessicator jar, it was sealed and incu-
bated at 30°C for 48 hours. At this time, all
colonies (0-300) were counted as in the total
aerobic counting procedure. The solid medium
eliminated the problem of drying which was en-
countered with a broth medium.
75
-------
TABLE 22. --ANALYTICAL SCHEDULE; FPI, SPI, SPE FOR EACH
WEEK OF CAMPAIGN; 1968-69.
Tot Tot Sol Tot Tot Sol- Org
Day sug CaO CaO BOD COD car acids Alk pH ids acids D. O.
Mon
Tues
Wed
Thurs
Fri
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Solids analysis included total solids, suspended solids, total dissolved
solids and settleable solids.
Total carbon analysis was completed on daily samples until about the
middle of campaign when a long period of inoperation of the carbon
analyzer necessitated the compositing of daily samples into weekly
samples for TOC.
Samples of FPI and SPE were taken by a mechanical sampler which drew
sample at the rate of about 50 ml/minute on a cycle which was sampled
from three to five minutes, every 20 minutes over a 24-hour period.
Samples of SPI were taken by a mechanical sampler which drew one
sample per hour over a 24-hour period.
For control purposes hourly pH readings of the SPE were taken by the
factory laboratory. Grab samples from FPI, SPI, SPE were ana-
lyzed for pH three times a day at eight hour intervals beginning each
morning at 8:00 a.m..
76
-------
TABLE 23. --ANALYTICAL SCHEDULE FOR EACH WEEK OF CAMPAIGN 1967-68.
Day
Tot
sug
Tot
CaO
Sol
CaO
BOD
COD
PH
Tot
c
FPI and
Mon*
Tues**
•Wed***
Thurs***
Fri*#*
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Tot Odor
C and Tot
filt color acids
SPE
XXX
XXX
XXX
'
NH3-N
X
X
X
P Alk
X
X
X X
X X
X X
Sol-
ids
X
X
X
APE****
Mon
Tues
Wed
Thurs
Fri
X
X
X
X
X
X
X
X
X
X
X
X
X
Condensed
Mon
Tues
Wed
Thurs
Fri
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Water Effluent*****
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
*Solids analyses included total solids, suspended solids, total volatile and suspended volatile
solids and settleable solids.
**A grab sample taken every 4 hours over a 16-hour period,
***A composite sample consisting of 8 individual samples taken at 1-hour intervals.
****A grab sample taken once a day.
composite sample taken over a 24-hour period by a mechanical sampler taking 1 sample
each hour. Analysis for dissolved oxygen was also completed on all 4 samples each week.
(From Complementary Study.)
-------
TABLE 24. --ANALYTICAL SCHEDULE FOR SAMPLES FOR
BIOLOGICAL ANALYSIS; SPI, SPE, APDC FOR
EACH WEEK OF CAMPAIGN 1968-69.
1.
2.
3.
4.
5.
6.
7.
8.
9.
PH
Total Sugar
Organic Acids
Total Acids
BOD5
COD
NO3-N
NO2-N
NH3-N
10.
11.
12.
13.
14.
15.
16.
17.
18.
PO4, Total, Ortho
S04=
so3 =
s=
Coliform
Fecal Streptococci
Total Aerobic Bacteria
Total Anaerobic bacteria
Solids (APDC)
Samples for biological analysis were taken twice per week and bio-
logical analysis was completed on both samples; chemical analysis was
completed on a composite sample from both days.
SPI and SPE samples were grab samples, but the anaerobic pond
sample was a depth composite.
The anaerobic pond depth composite was taken three days per week,
and all three samples were analyzed for all measurements except ni-
trogen, sulfur and phosphorous containing compounds.
TABLE 25. --ANALYTICAL SCHEDULE, FIRST POND MUD
SAMPLES, 1968-69-
1. Total Solids
2. Suspended Solids
3 . Total Carbon
4. Total CaO
5. Soluble CaO
6. Alkalinity
7. pH
8. Specific gravity (wet)
The mud samples were weekly composites made from the mud which
settled in an Imhoff cone from one liter of flume water. These were
from the 24-hour composite of the first pond influent.
The flume water was decanted, and then the mud was washed into a
collection jar with distilled water. All distilled water washings were
saved. The mud sample and washings were transferred to a volumetric
flask, heated slightly, cooled and made to volume after specific gravity
analysis was completed on a water decanted sample.
78
-------
TABLE 26.--PHYSICAL DATA SCHEDULE; 1968-69 CAMPAIGN
Temperature
1. First Pond Influent - Twice daily
2. Second Pond Effluent - Twice daily
3. Anaerobic Pond Depth - Once daily
4. Anaerobic Pond Effluent - Once daily
5. Condenser H^O - Once daily at river.
Charts*
1. First Pond Influent - Weekly flow chart
2. Second Pond Effluent - Daily pH chart
3. East Holding Pond Influent - Weekly flow chart
4. Flume System Overflow, factory - Daily flow chart
5. Condenser water, effluent - Weekly flow chart
Gauge and Meter Readings
1. Recirculation flow - Twice daily
2. Anaerobic Effluent** - Once daily
3. Anaerobic make up - Once daily
4. Anaerobic Pond Depth*** - Once daily
^Maintenance and calibrations were performed on a periodic schedule.
**Anaerobic pond effluent flow was calculated from gauge readings of a
Parshall flume.
:**Anaerobic pond depths were taken from a standing gauge.
79
-------
TABLE 27. --ANALYTICAL SCHEDULE, CONDENSER WATER AND MISCELLANEOUS FACTORY
EFFLUENTS IMPOUNDED FOR EACH WEEK OF CAMPAIGN 1968-69.
oo
o
Tot Tot Sol Tot Sol- Tot Org NH3 NO3 NO2
Day pH C BOD COD CaO CaO Sug ids acids acids D. O. N N N PO4
Condenser
Mon
Tues
Wed
Thurs
Fri
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Water
X
X
X
X
X
X
X
X
X
X
x (
x {
x {
X
Weekly )
Composite )
)
Miscellaneous Factory Effluents, Discharged to Holding Pond
Mon
Tues
Wed
Thurs
Fri
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
x (
x (
X (
X
Weekly )
Composite )
)
Solids analysis included total, suspended, dissolved and settleable solids.
Total carbon analysis was completed on daily samples until about the middle of campaign after
which the samples were weekly composites.
Nitrogen and phosphorus analysis were completed on weekly composite samples.
East holding pond samples were daily grab samples until about the middle of campaign, after
which these samples were taken by a mechanical sampler which took one sample every hour
over a 24-hour period.
Condenser samples were taken by a mechanical sampler which took one sample every hour, over
a 24-hour period, until about the middle of campaign after which they were daily grab samples.
-------
TABLE 28. --ANALYTICAL SCHEDULE; ANAEROBIC POND SAMPLES;
1967-68 POST CAMPAIGN; FEBRUARY 3 TO MARCH 28,
1968; THREE SAMPLES PER WEEK.
1. BOD
2. COD
3. D.O.
4. Temperature
5. pH
TABLE 29.--ANALYTICAL SCHEDULE (TWICE WEEKLY); ANAEROBIC
POND; 1968-69 POST CAMPAIGN; FEBRUARY 3 TO
MARCH 28, 1969.
1. pH
2. BOD5
3. COD
4. D.O.
5. Solids*
6. Organic Acids
7. Total Acids
8. Ammonia Nitrogen**
9- Nitrate Nitrogen**
10. Nitrite Nitrogen**
11. Sulfate
12. Sulfide
13. Phosphate, Soluble, Ortho**
14. Total CaO
15. Soluble CaO**
16. Pond Temperature
17. Pond Depth
18. Coliform***
19. Fecal Streptococci***
20. Total Anaerobic Bacteria***
21. Total Aerobic Bacteria***
*Solids analysis included only non-volatile suspended and dissolved
solids.
:*Analysis completed once per week on a composite sample made from
all separate samples taken during the week.
:*Analysis completed on two samples per week.
81
-------
TABLE 30. --ANALYTICAL SCHEDULE, ANAEROBIC POND SAMPLES;
1968-69 POST CAMPAIGN; APRIL 2 TO JULY 9, 1969;
ONE SAMPLE PER WEEK.
1. pH 11.
2. BOD5 12.
3. COD 13.
4. Solids* 14.
5. Organic Acids 15.
6. Total Acids 16.
7. Ammonia Nitrogen 17.
8. Nitrate plus Nitrite Nitrogen 18.
9. Sulfate 19.
10. Sulfide
Phosphate, Soluble, Ortho
Total CaO
Soluble CaO
Pond Temperature
Pond Depth
Coliform
Fecal Streptococci
Total Anaerobic Bacteria
Total Aerobic Bacteria
*Solids analysis included volatile and non-volatile, dissolved and
suspended solids.
TABLE 31 . .-ANALYTICAL SCHEDULE (WEEKLY); ANAEROBIC POND
SAMPLES; 1968-69 POST CAMPAIGN; JULY 17 TO
SEPTEMBERS, 1969-
1. pH 10.
2. BOD5 11.
3. COD 12.
4. Ammonia Nitrogen 13.
5. Phosphate, Soluble, Ortho 14.
6. Pond Temperature 15.
7. Pond Depth 16.
8. Solids*&** 17.
9. Organic Acids** 13.
Nitrate plus Nitrite Nitrogen**
Sulfide**
Total CaO**
Soluble CaO**
Coliform**
Fecal Streptococci**
Total Anaerobic Bacteria**
Total Aerobic Bacteria
Algae**
*Solids analysis included volatile and non-volatile, suspended and
dissolved solids.
**Completed on an occasional basis.
82
-------
CO
TABLE 32. --ANALYZED SUBSTANCES* ENTERING AND LEAVING THE FIRST AND SECOND
PONDS IN SERIES, SHOWING PERCENTAGE REMOVED BY THE PONDS PER
TON OF BEETS SLICED; 1968-69 CAMPAIGN AVERAGE.
Analyses
BOD
COD
Soluble CaO
Total CaO
Dissolved Solids
Total Carbon
Total Sugar***
Total Acids****(as CaO)
Organic Acids****(as CaO)
Pounds, per
ton of beets,
entering
first pond
2.76
2.77
0.61
1.40
3.13
2.03
2. 24
-
-
Reduction
(or increase)
across both
ponds
-2. 08**
-1.74
-0,34
-1.12
-1.68
-1.53
-1.93
+0.31
+0.59
Pounds, per
ton of beets,
residual in
pounds
0.68
1.03
0,27
0.28
1.45
0.50
0.31
0.42
0.52
%
reduction
75
63
56
80
54
75
86
-
— •
^Calculated on static pond volume basis and as if no physical loss and subsequent dilution
occurred.
**Minus sign designates reduction, plus sign designates increase.
***Calculated ssing periods characterized by high pond pH, where sugar concentration showed
a tendency to increase.
**##Increase across ponds approximately equal to residual in ponds, so no reduction occurred.
-------
TABLE 33. --PRIMARY POND INFLUENT, 1967-68 CAMPAIGN,
COMPOSITE SAMPLE ANALYSIS FOR BOD, COD, TOC, FIL-
TERED TOG, QRGANIC ACIDS, TOTAL CaO, SOLUBLE
CaOs ALKALINITY, pH.
Date
10-18
10-19
10-24
10-25
10-26
10-31
11-1
11-2
11-7
11-8
11-9
11-14
11-15
11-16
11-21
11-22
11-28
H-29
11-30
12-5
12-6
12-7
12-12
12-13
12-14
12-19
12-20
12-21
12-26
12-27
12-28
1-2
1-3
BODS* COD* TC
240
220
260
510
770
450
430
610
660
480
330
340
930
1,250
1,200
1,340
2,060
1, 510
1,430
1,250
1,240
1,280
930
530
1,
1,
1.
1.
1,
1,
1,
1,
1,
2,
1,
2,
5,
2,
1,
1,
1,
2,
2,
1,
.1,
1.
625
350
900
350
090
850
880
900
480
840
360
200
252
252
560
372
280
344
880
304
400
740
920
920
960
240
220
900
340
160
660
210
290
210
320
320
640
420
420
340
370
550
250
240
390
510
550
770
640
640
1,050
990
1,020
1,270
990
780
850
770
750
780
690
670
240
340
Filt
TC*
170
220
220
230
260
500
290
270
290
270
300
280
230
310
360
460
530
500
570
780
720
880
850
760
670
670
630
620
530
500
550
180
310
Org
Acids
370
240
140
330
280
360
390
430
290
280
280
520
520
520
600
520
530
470
480
470
310
310
Tot
CaO**
440
400
610
420
770
460
610
560
510
570
550
410
430
570
330
390
760
790
630
580
560
590
530
810
610
680
630
700
630
730
490
480
350
Sol
CaO**
270
320
440
450
460
320
320
370
380
380
371
370
350
170
340
280
370
440
500
310
320
340
520
520
520
600
520
530
470
480
470
310
310
Alk** pH
0
0
25
10
0
8
54
16
22
42
60
0
0
0
0
0
0
0
0
0
0
0
8.
7.
12.
12.
12.
9-
7.
12.
6.
7.
7.
7.
8.
10.
9.
10.
10.
11.
11.
11.
11.
11.
9.
10.
8.
8.
8.
8.
6.
6.
6.
9.
7.
0
2
2
2
4
4
4
4
9
1
4
2
6
8
6
5
9
9
7
6
4
8
0
3
5
4
0
0
6
8
5
0
0
*Parts per million
**Parts per million as CaO
84
-------
TABLE 3 3. --(continued)
Date
COD*
TC
Filt Org Tot Sol
TC* Acids CaO** CaO** Alk** pH
1-4
1-9
1-10
1-11
560
1,470
790
760
1,
1,
2,
500
660
260
000
300
690
450
390
270
650
350
380
300
340
350
330
410
340
450
350
300
340
330
340
0
0
0
0
7.
6.
7.
6.
8
3
0
5
*Parts per million
**Parts per million as CaO
TABLE 34. --DILUTION EFFECT ON pH IN PRIMARY POND OF FRESH
MAKE-UP WATER ADDED TO SYSTEM; 1967-68 CAMPAIGN.
Date
10-19
10-Z3
11-2
11-6
11-7
11-7
11-8
11-10
11-14
11-16
11-27
12-2
12-8
12-13
12-27
12-28
12-30
Hours of
dilution
8.0
8.. 0
8.0
4.0
7.0
6.0
1.5
4,0
7.0
16.0
7.0
10.0
3.0
4.5
7.0
16.0
14.5
Million
gallons
added
1. 18
0.36
0.52
0.42
1. 10
0.41
0.23
0.02
1.03
1.78
0.34
0.05
0.18
0.09
0.34
0.44
1.48
Lbs . lime
added/ hr.
275
600
600
150
150
150
150
300
300
425
515
150
100
400
200
200
200
Begin
pH
10.5
9.9
10.3
10.5
9.5
9.1
9.2
10.2
10.8
11.2
10.2
9.9
11.5
11.2
9.8
10.5
11.0
End
pH
9.5
8.5
9.7
9.2
8.6
8.0
8.4
9.8
9.1
9.4
9.6
9.8
9.3
9.0
9,0
9,0
9.0
85
-------
-------
APPENDIX III
TABLES
No.
35. Nalcolyte 670 Addition to Longmont Flume Water System 91
36. Goodland Spray-Cooled Condenser Water 95
37. Flash Cooler and Gas Washer Analysis, 1968-69
Campaign, Longmont Factory
96
38. Condenser Water, 1967-68 Campaign, and Miscellaneous
Factory Discharges 99
39. Condenser Water and East Holding Pond Influent,
Average Results, 1968-69 100
87
-------
-------
COMPLEMENTARY STUDY I
Effect of Polymer Flocculents on Fluming System
During the last month of the 1968-69 campaign the decision was reached
to test the affects of a polymer flocculent on the recirculated flume
water system. The objective of this study was to determine the affects
of the flocculent on pH control, settling efficiency, and bacteriological
activity.
Theoretically, the flocculents should increase settling efficiency by re-
moving a greater percentage of the smaller, collodial-like suspended
solids. If these solids were organic in nature, their removal would re-
duce the substrate for the bacteria to thrive on, therefore, less bacteria
and less organic acid production should result. It has been reported (36)
that certain bacteria types can be removed by utilizing settling aids.
Prior to this study bench scale tests were completed using Nalco
Chemical Company products to determine which flocculent would achieve
the best results in this system. The bench study indicated that of the
products tested, both Nalcolyte 670 and Nalcolyte 674 would achieve the
best results; both products would achieve comparable results at equi-
valent concentrations. Nalcolyte 670 was chosen as the flocculent to be
added to the flume water system because this flocculent can be made up
in a more concentrated stock solution than the Nalcolyte 674. Several
Calgon products were also tested on the bench and the results indicated
that Calgon 226 and Calgon 235 would work as well as the Nalco products
at comparable concentrations. Each of the flocculents used had been
cleared by the Food and Drug Administration for use in sugar refining
processes.
Three stainless steel tanks with about 175 gallon capacities and equipped
with propeller type mixers were utilized for mixing and aging the floc-
culent stock solution. The stock solution was prepared by using a special
dispersion funnel. The concentration of this solution was 0. 5 percent by
weight. The stock solution was pumped to a "header" which dispersed
the flocculent into the first pond influent just ahead of the mixing box.
Dilution water was added to the flocculent stream to achieve more dis-
persion of the flocculent before its entry into the fluming waters. The
ratio of dilution water to flocculent stock solution was greater than 1. 2 to
1 during the period in which 1 ppm flocculent was added and greater than
2. 4 to 1 when 0. 5 ppm was being added. For the first two days of this
study . 77 and . 80 ppm flocculent were added to the flume water and for
89
-------
the last 2 days 0.39 and 0.47 ppm.
Samples were taken at the first pond influent, second pond influent, and
second pond effluent by mechanical samplers operating over a 24-hour
period. These samples were analyzed for the following:
1. Clarity (Read as percent transmission on a Bausch and Lomb
"Spectronic 20" colorimeter. Sample was diluted 1:4 before
analysis.)
2. Control pH (pH taken from SPE by factory laboratory every hour
over a 24-hour period.)
3. Suspended solids (Analyzed by filtering sample through a tared
Gooch crucible with asbestos mat, drying and reweighing.)
4. Bacteria population (A once per day grab sample analyzed by
Department of Microbiology at Colorado State University at
Fort Collins, Colorado.)
Clarity
Previous to the flocculent addition the clarity at the SPI was 6. 3 percent
transmission and 3.5 percent at the SPE (Table 35). Upon the addition of
0. 77 ppm flocculent, the clarity at the SPI increased to 24. 2 percent; but
the clarity at the SPE remained low. It is thought that one day was neces-
sary to effectively treat all the system waters, as on the second day of
flocculent addition the clarity at both points was at about the 27-28 per-
cent level. Flocculent was added at a 0.80 ppm concentration the second
day.
Cutting the addition of flocculent added to the system in half had the effect
of lowering the clarity somewhat at both points. The improvement in
clarity upon the addition of flocculent indicated that the product increased
the settling efficiency of the system and removed a percentage of the fine,
collodial like suspended solids.
Suspended Solids
At the time this study was undertaken, both primary ponds were almost
full, and a larger than usual amount of suspended solids was being carried
over into the second pond. This time period was also characterized by
the formation of an unusually large amount of suspended solids in the
second pond by the formation of biological sludge, chemical precipitants,
etc.
90
-------
TABLE 35. --NALCOLYTE 670 ADDITION TO LONGMONT FLUME WATER SYSTEM
Day Number
Day ending date
Flocculent addition
ppm on flow
Suspended solids ppm
Percent transmission
1+3 solution
Settling efficiency
% difference susp sol**
Pounds susp solids
settled, first pond
Pounds increase
secondary pond
Pounds lime added
Control pH (SPE)
Bacterial numbers
(average in system)
1. Coliform mpn/ 100ml
2. Fecal strep lO^mpn/ 100ml
3. Aerobic 106mpn/ IQOml
4. Anaerobic lO^mpn/100 ml
1
1-21-69
0.00
FPI* '< SPI*
6,300 2,400
6.3
62. 0
145,700
14,300
7, 200
7.0
6,800
1.9
208
280
2
1-22-69
0.77
SPE* FPI SPI SPE
2,730 4,000 680 1,900
3.5 24.2 6.2
56.7 83.3 53.4
156, 800
56, 200
9,600
7.5
11,800
3. 1
120
380
*FPI - First Pond Influent; SPI - Second Pond Influent; SPE - Second Pond Effluent
**Calculated from FPI suspended solids less SPE suspended solids
-------
35. --(continued)
Day number
Day ending date
Flocculent addition
ppm on flow
Suspended solids ppm
Percent transmission
1+3 solution
Settling efficiency
% difference susp.sol.**
Pounds susp solids
settled, first pond
Pounds increase
secondary pond
Pounds lime added
Control pH SPE
Bacterial numbers
(average in system)
1. Coliform
mpn/ 100 ml
2. Fecal strep
10&mpn/ 100 ml
3. Aerobic
106mpn/100 ml
4. Anaerobic
106mpn/100 ml
3
1-23-69
0.80
FPI SPI SPE
2,300 670 670
27.0 28.0
71.2 70.9
72, 200
350
7,200
6.8
9, 600
3.8
420
420
4 5
1-24-69 1-25-69
0.47 0.39
FPI SPI SPE FPI SPI SPE
1,600 680 860 1,800 1,300
26.8 26.3 24.0 26.0
56.0 45.0 27.7
37,820 19,800
7, 600
7,200 7,200
6.8 6.8
73,300
2.9
52.5
190
-------
The addition of approximately . 80 ppm flocculent increased the removal
of suspended solids from 62 percent to approximately 70-80 percent and
effectively settled the equivalent of all suspended solids formed in the
second pond before discharge from the second pond, as suspended solids
concentration at the SPI and SPE were approximately equal on the second
day of 1 ppm addition. Cutting the flocculent addition in half lowered the
settling efficiency and raised the amount of solids being carried across
the second pond.
PH
The addition of flocculent in the specified concentrations did not affect a
significant rise in control pH at a fairly consistent level of lime addition.
Biological Propagation
The flocculent addition did not seriously hamper bacteriological propaga-
tion in the fluming waters.
Foam
The use of heated flume water and flocculent apparently produced a large
amount of foam which hampered fluming operations.
Conclusions
At a concentration of about .80 ppm of Nalcolyte 670 polymer flocculent
the settling efficiency and clarity of the flume water system were im-
proved significantly. However, when the addition was lowered to 0.5 ppm
the system efficiency and clarity decreased.
The addition of flocculent at the aforementioned concentration levels did
not effect a rise in control pH, at a lime addition rate of 300 to 400 pounds/
hour, or seriously inhibit bacterial propagation and activity.
The combination of heated flume water and flocculent apparently produced
unusually large amount of foam which hampered plant operation.
93
-------
COMPLEMENTARY STUDY II
Goodland Spray Cooled Condenser Water System
In the interest of total water pollution control, several miscellaneous
factory systems were sampled and analyzed. One of the systems studied
was the spray cooled recirculated condenser water system at the Great
Western sugar factory in Goodland, Kansas.
The hot condenser water from the factory flows into a receiving pond
after passing through typical spray heads used for evaporative cooling.
Grab samples were taken from the influent and effluent streams of this
pond twice during the 1968-69 sugar campaign.
Prior to the analysis of the Goodland spray pond samples, it was thought
that the solids and BODs in this type system might increase as campaign
progressed. However, the results of the analysis of the two sets of
grab samples, taken 22 days apart, do not show a build-up tendency when
the system was operating normally. Instead these samples show de-
creasing concentrations with respect to time (Table 36).
Phosphate was absent at both sampling periods and total inorganic nitrogen
measured was 14. 2 ppm into and 13. 1 out of the spray pond, the major
constituent being ammonia nitrogen. No major increases were noted
during the 22 day sampling interval in either contaminants or nutrients.
94
-------
TABLE 36.--GOODLAND SPRAY-COOLED CONDENSER WATER.
Spray pond
Sample Station influent
Temperature C°
pH
BODc ppm
COD ppm
Total sugar ppm
sucrose
Nitrate nitrogen
ppm
Nitrite nitrogen
ppm
Ammonia nitrogen
ppm
Phosphate, soluble,
ortho, ppm
Suspended solids
ppm
Dissolved solids
ppm
50
8.9
71
115
61
1. 1
0. 1
13
0
65
335
Spray p:ond
effluent
28
8.7
52
77
41
0.9
0.2
12
0
16
312
Spray pond
influent
52
8.2
12
62
0
0.7
0.3
13
0
0
178
Spray pond
effluent
31
8.7
15
39
0
0.9
0.3
15
0
0
202
95
-------
COMPLEMENTARY STUDY III
Gas Washer and Flash Cooler Water
Grab samples were taken from the gas washer and flash cooler effluents
at the Longmont factory and analyzed to determine the qualitative nature
of these waste streams. Positive conclusions cannot be drawn from one
sampling session, however, several results of this study should be
noted.
The main contaminant from the flash cooler appears to be ammonia
nitrogen, as BOD and COD levels were fairly low and phosphate was
absent (Table 37). The gas washer water appears to be low in nutrient
c one ent ration.
The large differential between COD and BOD concentrations in the gas
washer water would indicate that a large percentage of the carbonaceous
compounds were difficult to degrade biologically. The gas washer water
contained a large amount of carbon dioxide which probably formed in-
soluble carbonates in a limed environment.
TABLE 37.--FLASH COOLER AND GAS WASHER ANALYSIS, 1968-69
CAMPAIGN, LONGMONT FACTORY.
Sample station
pH
BODc ppm
COD ppm
Dissolved oxygen ppm
Ammonia nitrogen ppm.
Nitrate nitrogen ppm
Nitrite nitrogen ppm
Phosphate, soluble, ortho, ppm
Carbon dioxide ppm
Suspended solids ppm
Dissolved solids ppm
12-26-68
11-19-68
Flash cooler Gas washer
9.0
47
54
48
2.1
0.1
0
85
849
6.
11
65
6.
5
1.
0.
0
551
-89
720
0
2
5
1
96
-------
COMPLEMENTARY STUDY IV
Foam Control
The recirculated flume water system produced large amounts of foam
when control pH was high (10.0-12,0) and lesser amounts when control
pH was low { <10<,0). The foam presented a problem in the flumes and
in the beet laboratory tare house.
The foam was controlled in the tare house by injecting Exfoam 440, a
product of the Dearborn Chemical Division of W= R0 Grace and Company,
into the tare house influent flow with a positive pressure pump. Approxi-
mately 3 gallons per day of this product was used for foam control.
Several other defoaming agents were used successfully for foam control
in the overall flume water system. These products were:
Name
Manufacturer
Amount
gallons/day
1. Hodag PX 88 Hodag Chemical Co. 25
2. Mazu 103 Mazer Chemical Co. 25
97
-------
TABLE 39.--CONDENSER WATER AND EAST HOLDING POND
INFLUENT, AVERAGE RESULTS, 1968-69.
Condenser Water
PH
BOD 5 ppm
COD ppm
Dissolved
oxygen ppm
Soluble CaO ppm
Total CaO ppm
Total sugar
Ppm sucrose
Settleable
solids ml/L
Dissolved
solids ppm
Suspended
solids ppm
Total acids
ppm CaO
Organic acids
ppm acetic
NH3-N ppm
NO3-N ppm
NO^-N ppm
Phosphate
ppm ortho
Temperature °C
Flow gpm
Total carbon
ppm
High
8.9
72
206
6.5
547
1,349
35
0.4
1, 128
368
546
__
18
1.4
0.7
0.5
49
7, 732
160
Low
7-9
3
3
3.0
203
217
—
550
__
217
--
--
0.9
0.1
--
21
5,398
Average
8.6
21
44
4.6
315
346
5.5
.02
836
36
296
--
9
1.0
0.4
.05
38
6,569
60
East holding
pond influent
High
12.8
14, 968
164,409
5. 1
3,503
6,055
32, 740
50.0
61, 178
11, 813
2,729
2,338
82
50. 1
2.9
19.8
57
281
29, 100
Low Average
6.4
170 2,
353 4,
0.0
179 1,
394 2,
0.0 3,
0.8
1,056 1,
88 6,
156
0.0
0.0
0.50
0. 12
2.0
15
133
240 1,
12.
959
715
0.
061
027
671
21.
866
664
590
446
22
14.
1.
8.
30
190
641
0
6
5
8
0
3
100
-------
SELECTED WATER
RESOURCES ABSTRACTS
INPUT TRANSACTION FORM
1. '-Report No.
w
IS.
Biological Treatment of Concentrated Sugar Beet
Wastes
James H. Fischer
Beet Sugar Development Foundation
P.O. Box 1546
Fort Collins, Colorado 80521
12060 FAK
Environmental Protection Agency report number, EPA-660/2-7^-028, June
A study of the variables influencing a closed loop recirculating flume water
system for conveying sugarbeets for processing was conducted at Longmont,
Colorado. Settleable solids were removed by screening, addition of milk
of lime and settling; the concentration of dissolved solids increased daily
during the processing season. The increasing concentration caused no problem
provided the pH was 10 or.greater and that the water temperature did not
exceed 20°C. A deep anaerobic pond received surplus system waters and the
total system waters when operations ceased. Anaerobic digestion was aided by
addition of nutrients and odors reduced by surface aeration. Water eventually
met discharge standards, and was used the second year to fill the system.
Wastewater Treatment, Water Reuse, Wastewater Quality Control, Reclaimed
Water, Pollution Abatement, Recirculating Treatment Facility, Industrial
Waste Treatment.
Sugarbeet waste treatment, High solids flume water, Suspended solids
separation, Concentrated dissolved solids, Anaerobic digestion.
Send To:
WATER RESOURCES SCIENTIFIC INFORMATION CENTER
U.S. DEPARTMENT OF THE INTERIOR
WASHINGTON, D.C. 20240
Fischer,.James H.
Beet Sugar Development Foundation
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