FEBRUARY 1973 Environmental Protection Technology Series
Anaerobic - Aerobic
Ponds for Beet Sugar
Waste Treatment
Office of Research and Monitoring
U.S. Environmental Protection Agency
Washington, D.C. 20460
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and
Monitoring, Environmental Protection Agency, have
been grouped into five series. These five broad
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development and application of environmental
technology. Elimination of traditional grouping
was, consciously planned to foster technology
transfer and a maximum interface in related
fields. The five aeries are;
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Environmental Health Effects Research
Environmental Protection Technology
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sociaeocmomic Environmental studies
^KQ£SCTSaN .: ^Oft
th ENVIRONMENTAL
J ^iSiff seizes
and
*TO^|^^fe fljouroes i of
re control and treatment
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EPA-R2-73-025
February 1973
ANAEROBIC-AEROBIC PONDS FOR BEET
SUGAR WASTE TREATMENT
By
William J. Oswald
Ronald A. Tsugita
Clarence G. Golueke
Robert C. Cooper
Grant Nos. WPD 93-03 and 93-04
Project Officer
* James R. Boydston
Environmental Protection Agency
National Environmental Research Center
Corvallis, Oregon 97330
Prepared for
OFFICE OF RESEARCH AND MONITORING
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
For sale by tho Superintendent of Documents, U.S. Government Printing Office, Washington, D.C. 20402
Price $2.10 domestic postpaid or $1.75 QPO Bookstore
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EPA Review Notice
This report has been reviewed by the Environmental Protection
Agency and approved for publication. Approval does not sig-
nify that the contents necessarily reflect the views and
policies of the Environmental Protection Agency, nor does
mention of trade names or commercial products constitute
endorsement or recommendations for use.
11
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ABSTRACT
Sugarbeet factory transport (flume) water wastes were treated
in pilot-sized anaerobic, facultative and aerobic ponds. Phy-
sical, chemical and mechanical data were collected on the
performance of each pond which showed cause for abandoning
the facultative phase of treating. BOD removal in the anaero-
bic pond was a linear function of the BOD loading and up to
a loading of 2,000 pounds of BOD per acre per day, 80%
removal was accomplished with the assistance of mechanical
aeration. The algae (aerobic) pond was mixed by means of
four 12,000 gpm propeller pumps. Some unseparated algae pond
effluent was recycled to the anaerobic pond providing organic
nitrogen, phosphorus and "seed" for the microbial transfor-
mations. Additional nutrients were required for maximum
performance. The system was effective in converting solu-
ble BOD to insoluble BOD and, had filtration or separation
been applied to effluents, BOD removal would have been 98
percent. Loadings above 1,000 pounds of BOD per acre per
day generally are not permissible because of odor production
and high effluent BOD.
Key Words: Sugarbeet wastes, anaerobic pond, facultative
pond, aerobic pond, algal growth, nutrient
addition, odor control
111
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CONTENTS
Section
I Conclusions
II Recommendations
III Introduction
IV Experimental
The Pilot System
Experimental Program
Observations and Analyses
Sampling Techniques
V Results
General Waste Characteristics
Photosynthesis and Respiration
Floating Aerator Study
Anaerobic with Aeration Followed by
Facultative Pond
Anaerobic with Aeration Followed by
Algae Pond
Environmental Conditions
Flows
Loadings
Physical Characteristics of Liquids
PH
Solids
Conductivity
Light Penetration
Chemical Changes
Nutrients
Nitrogen
Organisms
Gas Production
Nutrient Studies
VI Discussion
VII Acknowledgments
VIII References
IX Glossary
X Appendices
1
3
5
11
11
13
14
15
21
21
21
23
25
26
29
30
31
37
37
40
47
48
48
58
61
67
73
76
79
95
97
99
101
v
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FIGURES
No.
1. Showing Layout of Ponds, Arrangement of
Baffles and Mixing Pumps in Aerobic Pond
2. Mixing Pump Installation for Algae Pond-Tracy
3. Baffle Detail - Beet Sugar Development
Foundation Algae Pond-Tracy
4. Bronson Gas Collector
5. Schematic Diagram of System as Applied in
Aerated Anaerobic Plus Mixed Algae Pond Series
6. Dissolved Oxygen vs Time of Day
7. Change in COD, BOD and D.O. in Anaerobic Pond
During Sustained Aeration with 5 H.P. Floating
Surface Aerator
8. Mean Visible Solar Energy and Surface Water
Temperature, Maximum and Minimum Air Temperature
as a Function of Month
9. Monthly Mean Values for Unfiltered BOD as a
Function of Pond and Month
10. Extremes and Central Tendency pH Relationship
in Influent/ Anaerobic and Algae Pond as a
Function of Month
11. Monthly Mean, Maximum, and Minimum Dissolved
Oxygen Values for Algae Ponds Daily at 3 P.M.
12. Monthly Mean Dissolved Volatile Solids as a
Function of Pond and Month
13. Monthly Mean Dissolved Ash as a Function of
Pond and Month
14. Monthly Mean Suspended Volatile Solids as a
Function of Pond and Month
15. Monthly Mean Packed Volume of Centrifuged
Solids as a Function of Pond and Month
16. Monthly Mean Suspended Ash as a Function of
Pond and Month
11
12
13
16
18
23
24
29
35
38
39
42
43
44
45
46
vi
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17. Monthly Mean Conductivity as a Function of
Pond and Month 47
18. Monthly Mean Light Penetration as a Function
of Pond and Month 49
19. Monthly Mean Magnesium Concentration as a
Function of Pond and Month 49
20. Monthly Mean Calcium Concentration as a
Function of Pond and Month 50
21. Monthly Mean Values for Sulfate as a Function
of Pond and Month 52
22. Sulfate Reduction in Anaerobic Pond as a
Function of Temperature 53
23. Monthly Mean Dissolved Sulfides as a Function
of Month 54
24. Dissolved Sulfides as a Function of Absorbed
BOD Load 56
25. Mean Odor Product as a Function of Month for
Influent, Anaerobic and Algae Ponds 56
26. Monthly Mean Odor Product as a Function of
Monthly Mean Dissolved Sulfides 57
27. Monthly Mean Organoleptic Odor Product as a
Function of Applied Areal Loading 59
28. Monthly Mean Values for Unfiltered COD as a
Function of Pond and Month 60
29. Monthly Mean Values for Filtered COD as a
Function of Pond and Month 60
30. Ratio of Monthly Mean Filtered to Unfiltered
COD as a Function of Pond and Month 61
31. Monthly Mean Total Nitrogen Values as a Function
of Pond and Month 63
32.
Monthly Mean Values for Nitrate Nitrogen as
a Function of Pond and Month
64
VII
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33. Monthly Mean Values for Ammonia Nitrogen as
a Function of Pond and Month 65
34. Monthly Mean Values for Organic + Nitrite
Nitrogen as a Function of Pond and Month 66
35. Monthly Mean Algae Counts as a Function of
Pond and Month 69
36. Monthly Mean Packed Volume of Centrifuged
Algal Solids as a Function of Month and Pond 70
37. Observed Daphnia and Daphnia-Like Organisms
Per Liter as a Function of Pond and Month 72
38. Monthly Mean Rotifer Counts as a Function of
Pond and Depth 72
39. Monthly Mean Purple Sulfur Bacteria Count
as a Function of Pond and Month 74
40. Relationship Between Gas Production and
Temperature for Various Months 74
41. Monthly Mean BOD of Algae or Facultative Ponds
as a Function of BOD and Filtration 82
42. Main Waste Ponding Area Required for 4.5 K
Ton Factory 85
viii
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TABLES
Page
1. Operating Depths for Ponds During July - Dec.
1968 Runs 19
2. Mean Values for Certain Analytical Parameters
of Holly-Tracy Plume Water - 1965 - 1968 22
3. 1967 Aerated Anaerobic Pond Plus Facultative
Pond with No Recirculation 27
4. Summary of Mean Monthly Plow Values for In-
fluent Recycle, Transfer and Effluent Waste
Streams 32
5. Summary of Monthly Mean COD and BOD Values as
a Function of Pond and Month 33
6. Monthly Mean Flows BOD Values and Performance
Data for Anaerobic-Algae Pond in Series 36
7. Summary of Solids Data 41
8. Summary of Monthly Mean Nitrogen Values as a
Function of Species, Pond and Month - All
Values Mg Per Liter as N 62
9. Nutrient Relationships 68
10. Algal Species in the Ponds and the Percentage
of Samples Examined in Which They Occurred
as a Function of Pond and Month 75
11. Nutrient Spiking Experiment 77
IX
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SECTION I
CONCLUSIONS
Because of the large quantities of mud and extraneous vege-
tation contained in beet flume water, screening and short-
term sedimentation are absolute requirements for pretreatment
of sugarbeet waste. The degree of sedimentation should be
limited in time to a few hours, however, since carry-over
of some mud seems to have a beneficial effect on fermentation
in an anaerobic beet waste pond.
Even after screening and short-term sedimentation, sugarbeet
waste is so variable in pH, BOD, and composition that short
detention period biological processes such as activated sludge,
trickling filter, and algae ponds cannot be effectively em-
ployed as the initial process in a treatment system.
With mechanical surface aeration at about 300 Ibs of 02 per
day, an anaerobic pond 14 ft deep and one acre in surface
area may be loaded at a rate of 1000 Ibs of ultimate BOD per
acre per day without excessive odor.
When factory waste is passed through an anaerobic pond, the
discharge has a more uniform pH and a much lower and more
uniform BOD than does the original waste. In spite of its
lower biodegradeability, it is by virtue of its uniformity,
more subject to effective short detention time secondary
biological treatment.
Following passage of waste through an anaerobic pond, the
pond effluents are devoid of oxygen, high in a turbidity
consisting of microorganism and colloidal-reduced substances
such as metal sulfides, high in BOD, and are malodorous.
Effluents of this quality must be subjected to aeration
treatment before storage, discharge to the aquatic environ-
ment or reuse.
Aerobic treatment subsequent to adequate anaerobic ponding
may involve photosynthetic oxygenation, simple ponding in a
facultative pond, or possibly mechanical aeration. The last
alternative has not been extensively explored. In the case
of photosynthetic oxygenation with algae removal, loadings
of 200 Ibs of ultimate BOD per acre per day would be accep-
table, whereas in the case of facultative ponds, without
algae removal, loadings of 100 Ibs of ultimate BOD per acre
per day are the most that can be recommended because of odors.
In the case of mechanical aeration, it seems likely that to
maintain a 4 mg per liter DO residual, 1 horsepower would
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be required for each 40 Ibs of daily ultimate BOD applied
to the aeration pond.
As shown in Figure 6, recirculation of secondary pond efflu-
ent to the anaerobic pond influent probably had a beneficial
effect upon overall treatment. The effect probably is related
to nutrient return and "seeding". A recirculation rate of h
to 1 Q should be adequate to achieve these benefits.
If recovered waste water from an aeration pond is to be ren-
dered suitable for discharge to the aquatic environment or
for recycle and reuse in a beet sugar factory, it should be
subjected to filtration or separation to remove clay tur-
bidity and bacterial and algae cells. The removal of these
substances following anaerobic-aerobic treatment produces a
final effluent of fairly high quality having a BOD of less
than 2 mg per liter. Following passage through the anaerobic
pond, nutrient supplementation with ammonium-nitrogen at 20
mg per liter and phosphate at about 10 mg per liter is essen-
tial for adequate aerobic biological treatment. Because of
losses of nitrogen which were found to be substantial in the
anaerobic pond, nitrogen should be added following passage of
the liquid through the anaerobic pond. The best point for
addition of phosphate requires additional study.
Treatment to remove dissolved nutrients will not be required
if nutrient supplementation is carefully controlled. However,
to meet the quality standards set up by most of the states,
suspended solids will have to be removed from the final efflu-
ent by filtration or by some other separation device prior
to discharging the effluent into the environment.
The problem of odors in beet waste ponds can only be solved
by avoiding overloading of ponds, by providing sufficient
treatment area, sufficient aeration, and by providing nutrient
supplementation. Anaerobic pond loadings should not exceed
1000 Ibs per acre per day, and aeration should be applied at
the surface of the anaerobic pond to the extent required to
prevent odors. Secondary aerobic ponds should be loaded at
not more than 200 Ibs per acre per day, and supplementary
aeration in the form of flow mixing or possibly surface
aerators should be provided. Final effluent must be fil-
tered or otherwise separated to produce a clear supernatant
if it is to be suitable to meet most discharge requirements.
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SECTION II
RECOMMENDATIONS
A full-scale project should now be developed in California
to handle the entire output of a 4 to 5 K-ton factory to
demonstrate the feasibility of anaerobic-aerobic ponding for
nuisance-free treatment of beet sugar factory wastes. The
system should include prescreening and short-term sedimenta-
tion, anaerobic ponding with maximum loads at 1000 Ibs per
acre per day, and have surface aeration for odor control. The
anaerobic pond should be followed by aeration systems which
include aerobic ponds at loadings of about 200 Ibs per acre
per day. In the aerobic ponds a regimen of eddy diffusion,
supplementary aeration, and photosynthetic oxygenation should
be applied. Recirculation of secondary effluent to the in-
fluent should be supplied. The system should include screen-
ing of recycled water, nutrient supplementation in the algae
or aeration pond, and filtration of final effluent. Data
collection should include all parameters in this study and in
addition those pertaining to chlorides and alkalinity. The
system should be installed in a factory which does not produce
Steffens waste, and which has separate disposal of all human
wastes.
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SECTION III
INTRODUCTION
HISTORICAL
The first of this series of two studies of large-scale pilot
plant treatment of beet sugar flume water waste was initiated
on June 1, 1965 and terminated on May 31, 1967. The second
study, to be summarized in this report, was initiated on June
1, 1967 and was terminated on May 31, 1969. The major objec-
tive of the 1965 to 1967 study was to demonstrate the feasi-
bility of utilizing a series of three ponds "anaerobic",
"facultative", and "algae" to stabilize beet sugar factory
waste water by decreasing the odor of waste ponding and ren-
dering the final effluent sufficiently low in BOD for dis-
charge to the aquatic environment. To accomplish this demon-
stration, a six-acre pilot plant was constructed at the Holly
Sugar factory, Tracy, California. The pilot plant consisted
of a pumping station, a screening system, a settling tank, a
metering station, a one-acre by 14 ft deep anaerobic pond, a
two-acre by seven-ft deep facultative pond, and a three-acre
by three-ft deep algae pond. A description of this pilot plant
and of the operational data are given in detail in Progress
Report III (1) which covered the first series for the period
June 1, 1965 to May 31, 1967. Inasmuch as this report is
intended to cover only the 21-month period, June 1, 1967 to
March 1, 1969, information given in Progress Report III will
be repeated only as required for clarity.
One of the conclusions of Progress Report III was that it is
not possible to operate a ponding system for flume water wastes
without odor in the absence of relatively large quantities of
molecular oxygen. Thus, it was concluded that systems involv-
ing aeration by mechanical aerators or by photosynthetic oxy-
genation should be investigated. The second series of studies
involved an exploration of these alternatives.
PREVIOUS WORK
The work done in the first research period was mostly concerned
with the anaerobic phase of the anaerobic-facultative-aerobic
lagoon complex, and hence the research was directed towards
determining the extent of treatment that could be accomplished
without special design features to emphasize aeration or algal
production. In line with this emphasis, operational features
such as loading and recirculation and their relationship to
treatment efficiency were extensively studied.
Results obtained in the research, cf. Progress Report III (1)
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and Tsugita, et al. (2), furnished ample evidence for believ-
ing that the basic" principles involved in treatment of sugar-
beet waste waters by lagooning in an anaerobic-facultative-
aerobic lagoon complex are applicable to real systems, but by
no means constitute an optimum system. For example, conflic-
ting information was obtained on recirculation. The importance
of recirculation is primarily related to conveyance of oxygen,
"seed", and nutrients into the primary stages of the system;
in dilution of the influent waste with recovered water; and,
in forcing stronger wastes forward in the system, thus possibly
increasing the efficiency of secondary units. There is some
evidence from the initial studies that the optimum rate of
recirculation changes with changing conditions in the ponds;
and that under some conditions, rates in excess of one or two
times the influent volume may be undesirable. The results
further indicated that a controllable growth of algae in the
aerobic pond is dependent either on controlled mixing or on
some presently unknown factor.
Despite generally favorable results, the three-pond system as
it was applied in the first study would not be suitable for a
routine application to factory wastes simply because waste
treatment was not accomplished to the extent required for an
odor-free operation, or for an operation in which an effluent
would have to meet reasonably strict discharge requirements.
The reason for these shortcomings can to some extent be ascer-
tained from a consideration of the results. Most of the BOD,
COD, nitrogen, and other removals were accomplished in the
anaerobic pond; whereas the facultative and aerobic ponds con-
tributed only slightly to the total treatment and thus were
apparently underloaded. While substantial, the extent of
treatment accomplished in the anaerobic pond was far from that
needed for full treatment to an effluent acceptable in the
aquatic environment. However, had the remaining two ponds been
operating at their potential capacities, the total treatment
undoubtedly would have been satisfactoryjudging from the past
experience with such pond systems in domestic waste treatment.
A question thus remained: Why did the facultative and aerobic
ponds apparently fail to make a substantial contribution to
treatment? Another problem was that algae failed to grow under
certain conditions prevailing in the ponds in which they were
supposed to grow, thus limiting oxygenation. As the system
was designed to operate, algae were to fill a very important
role in that they were to supply the oxygen removed in the
aerobic pond and in the surface strata of the facultative
pond. Availability of photosynthetic oxygen would have made
possible a degree of BOD removal not possible in the absence
of oxygen. (An additional function of algae was intended to
be the removal of algal nutrients and their return with recir-
culant to the anaerobic pond.) The answer to the question -
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why the algae failed to grow in sufficient quantity - is
believed to be due to a lack of certain required nutrients
and obstruction of light by bacterial and sulfide turbidity,
as well as an absence of mixing.
In the first two years of research, no provision was made
either to provide special nutrients or for mixing the algae-
producing or aerobic pond, although past experience with
sewage ponds furnished definite reasons for believing mixing
is an important factor in algae growth and production. How-
ever, inasmuch as the evidence for the need to mix had not
been demonstrated in the case of beet sugar flume wastes, and
inasmuch as the aim in designing any industrial waste treat-
ment system is to attain satisfactory performance at a minimum
capital and operational cost, provision for mixing the aerobic
pond was deliberately omitted in the first design in the hope
that it might not be essential. It was also considered desir-
able to learn just what could be accomplished without mixing.
Experience gained in the prior studies with domestic sewage
had indicated that although algae grow in ponds without mixing,
mixing is essential to the sustained and controlled production
of algae.
A further consideration of the first period results brought
to light several important pieces of information lacking in
the research, and which had to be obtained in these studies
if full utilization of the system were to be attained in
practice. For example, more information was needed about
the sensitivity of the principal microorganisms involved in
the process, i.e., their environmental limits; about the mech-
anism of coliform and pathogen die-off; about the mode of S0^=
removalwhether or not it is biological, chemical, or physical,
or a combination of these, and about the factors involved in
odor elimination and COD and EOD reduction. It was also deemed
important to determine the independent role of the facultative
pond in the system and the independent role of the algae pond.
Inasmuch as the results obtained in the first research period
indicated that the satisfactory performance of the facultative-
aerobic phases is essential to the efficient function of the
anaerobic-facultative-aerobic complex as a whole, the prin-
cipal objective of the proposed research was to determine the
effectiveness of the system with either the facultative or the
aerobic ponds operating in series with the primary or anaero-
bic pond. Also, because one of the functions of the secondary
ponds is aeration, a study of mechanical aeration as compared
with natural aeration was deemed desirable.
Experience in other studies of natural aeration as well as
that gained in the first study period without mechanical
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aeration showed that algae constitute an important feature
in the anaerobic-facultative-aerobic lagooning system for
treating any waste, and particularly sugarbeet waste waters,
and that algae cannot be produced in the quantity required
to fulfill their role without at least a minimal provision
for mixing the aerobic pond. Because of the importance of
these two (algae production and mixing), another objective
of the study was the determination of the effect of mixing
and, of course, other environmental factors on algae produc-
tion in the system, as well as the consequent effect on the
treatment performance of the complete pond complex.
Among the specific operational factors considered for study
with respect to the system as a whole and to its constituent
units were recirculation rate and flow pattern, mixing velo-
city, frequency and duration, retention period, depth, and
point of introduction of influent and removal of effluent.
However, because of operational difficulties and time limi-
tations, it was not feasible to explore all of these factors.
No attempt was made to vary natural environmental factors,
but data were collected on light, temperature, and solar energy
so that correlations could be made between observed natural
factors and accompanying system performance should corre-
lations exist.
Beet sugar flume water is a waste of moderate strength and
high variability. Studies made in the first re-search period
showed that it is high in carbon and BOD, that the 5-day
BOD is about 67 percent of the COD, indicating a relatively
high biodegradability of the nutrients. The waste is often
deficient in nitrogen and phosphorus and consequently is
often moderately slow to decompose biologically. The waste
may contain artificially introduced compounds specifically
designed to retard biological growths, particularly when
cooling towers are employed for condenser water and conden-
sate is included in the waste stream. The waste always
contains substances which become volatile and malodorous
during anaerobic decomposition. Under anaerobic conditions,
hydrogen sulfide is often emitted. Moreover, judging from
the odors, volatile acids, alcohols and other aromatic sub-
stances are characteristically produced.
Many beet sugar factories in a warm climate such as prevails
in California and Texas have two operational periods (cam-
paigns) of about four months each year; whereas, factories
in cold climates such as are characteristic of Colorado and
Idaho have a single yearly campaign beginning in October and
extending through March. During the fall in warm climates and
during the winter and spring in cold climates, stockpiled
beets rot and release organic matter as compared to that tak-
ing place with fresh beets. The release of organic matter
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results in an increased strength of the wastes. Regardless
of climate, start-up problems are always encountered.
Processing capacities of modern beet sugar factories range
from 1,000 to 10,000 tons of beets per day. For each ton
of beets processed, from 500 to 2,000 gallons of excess
water containing 500 to 2,000 mg per liter of BOD are pro-
duced. Highest BOD values are associated with greatest
reuse of water. Hence, factories which discharge only 500
gallons per ton of beets may have waste waters of 2,000 mg
per liter BOD; whereas factories which discharge 2,000 gal-
lons per ton of beets may have wastes of 500 mg per liter
BOD. Depending on operations and time of year, a beet sugar
factory may waste from 5 to 20 Ibs of BOD in flume water per
ton of slice, the average probably being about 8 Ibs. Thus,
a factory slicing 4.5 kiloton {about average), will discharge
36,000 Ibs of BOD per day.
NATURAL SURFACE AERATION
In a quiet pond, natural surface aeration will contribute
about 20 Ibs of oxygen per acre per day to the impounded
water. If one were to assume that beet sugar flume water
were as easily treatable as domestic sewage (which is
decidedly not the case), one would expect the aerial require-
ment for simple surface aerated ponds to be on the order of
0.40 acres per ton of slice. Thus, an average factory with
4.5 KT of slice would require about 1,800 acres of natural
disposal area. If this area or its equivalent in designed
facilities were not provided by the factory and the wastes
were put into the natural aquatic environment, at least
1,800 acres of that environment would undergo some degree
of dispoilment and all opportunity for. water reclamation
would be lost. If the area of land dispoiled is to be
decreased, a more sophisticated means of aeration or treat-
ment would be required. Water losses due to evaporation and
percolation depend upon local conditions such as rainfall,
evaporation, and soil characteristics. However, such losses
usually amount to about 2 million gallons per acre per year,
and hence in the case of an 1,800 acre pond, losses would
exceed the loading velocity for this rate which would be
about 0.58 million gallons per acre per year. Thus, if ponds
were built of sufficient size to permit natural aeration to
satisfy the applied BOD, they would be so large as to remain
dry and non-operational much of the year. On the other hand,
if it is assumed that the hydraulic loading were sufficiently
large to insure that the ponds would be wet the year around,
the areal requirement could be reduced to 0.115 acres per ton
of slice; and the corresponding oxygenation load would average
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70 Ibs per acre per day with peaks up to 110 Ibs per acre
per day. This degree of loading would far exceed the rate
of natural aeration and consequently would demand a contri-
bution of oxygen from external sources at rates on the order
of 50 to 90 Ibs per acre per day. Such a contribution is
feasible from natural photosynthesis provided light and
temperature permit. It probably is the maximum that can be
attained without special provision for mixing and other
treatments. If land use is to be further curtailed, special
systems must be employed.
In summary, the work done previously has shown that substan-
tial reductions in solids, BOD, and nutrients may be attained
in simple ponds; but that land use, effluent BOD and odor
would be excessive. On the other hand, the first series of
studies showed that by using an anaerobic pond in series
with other ponds, land use could be curtailed. However,
effluent BOD and process odor would still be excessive.
The specific purpose of this second study was to explore
mechanisms to improve pond design and operation to increase
the rates of BOD and odor removal and to further explore
methods of decreasing land requirements. Another purpose
of the work was to derive design criteria for systems of
ponds which would have predictably satisfactory performance
over a range of environmental conditions; and which could
therefore be applied to meet discharge specifications in a
variety of climates.
10
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SECTION IV
EXPERIMENTAL
During the 1967 to 1969 period, three types of systems were
studied: an anaerobic pond with aeration, an anaerobic pond
with aeration in series with a facultative pond, and an
anaerobic pond with aeration in series with a photosynthetic
algae pond.
THE PILOT SYSTEM
A detailed description of the overall system including copies
of the original blue prints was presented in Progress Report
III (1) and modifications of the system for the anaerobic,
the anaerobic-facultative, and the anaerobic-algae system to
be reported herein are shown in Figure 1.
4-12,000 gpm, I' TDH
IOH.R eocMSee ''9- 2 fordetoilsi
FACULTATIVE POND HE
NOT USED IN JULY-DEC. 1968
STUDIES
s-
Q = 48,000 GPM -4 _,
/"^^ man ~
( ~\
^*- 4'HIGH BAFFLESISee Fig. 3 for details) v
r )
* AEROBIC POND BT -*<
( J
\^ -2r~^ MIXINfi PIIMP^'1^ ^-
4
^
}
s
OPERATING SEQUENCE: Aug 1967-H only
Fall 1967-H plus
Soring 1966- n plus ET
Foil 1968- E plus IE
FIGURE 1. SHOWING LAYOUT OF PONDS, ARRANGEMENT OF BAFFLES
AND MIXING PUMPS IN AEROBIC POND
In brief, as shown in Figure 1, following DSM screening and
one to two hours of sedimentation, waste was introduced into
the anaerobic pond together with recirculant, and then was
discharged into either the facultative or into the elongated
mixing pond at the discharge end of the mixing pumps and
because the three pond regimen had been explored previously
11
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in Progress Report III. During tests with the anaerobic-
facultative system, recirculation was not used because the
algae pond was out of operation.
The low-head propeller pumps used to mix the algae pond
Were designed for 12,000 gallons per minute each and are
shown schematically in Figure 2. The four propeller pumps
require about 40 HP to recycle and maintain algae in sus-
pension and theoretically to provide nutrients for algae
from the water soil interface, where facultative bacterial
action is near its maximum, and to prevent thermal strati-
fication. Details of the baffle construction designed to
provide uniform flow in the algae pond are shown in Figure 3
4-IB" PROPELLER PUMPS
Q'12,000 GPM
-------
2"x6" CORNICE
PIPE STRAPS
PLATE STRAPS
V.
V
SHEATH ONE SIDE
WITH GALVANIZED
CORREGATED IRON
-2"x4" BRACE
^ DIAMETER 7' LENGTH
BLACK PIPE @ 6' CENTERS
3'
SCALE : I"--1-0"
6'
FIGURE 3. BAFFLE DETAIL - BEET SUGAR DEVELOPMENT FOUNDATION
ALGAE POND-TRACY
EXPERIMENTAL PROGRAM
In the current series the anaerobic pond was first operated
alone in conjunction with a surface aerator (Welles Products
Corporation) for several weeks during the summer period of
1967. Although the factory was not in operation at this
time, the pond had retained a substantial amount of oxidize-
able organic matter from the spring campaign. Treatment
had to be restricted to the anaerobic pond because the algae
pond had to be taken out of operation for drying in order
to construct the baffles and mixing pump station described
in the preceding paragraphs.
When factory wastes became available during the 1967 fall
campaign, drying and reconstruction of the algae pond had
not been complete. Therefore, an anaerobic-algal pond plus
facultative system was operated for the balance of the 1967
fall campaign. The facultative pond shown dotted in Figure
1 was used. In the spring of 1968, experiments were con-
ducted with the surface-aerated anaerobic pond in series
with a pump-mixed, high-rate algal pond. It was found that
severe leakage occurred under the baffles of the algal growth
pond, and consequently, the system was modified during the
summer of 1968 to prevent leakage and improve the flow pattern.
13
-------
Another complication occurred in the summer of 1968 in that
the Holly Sugar Company found it necessary to construct
new ponds to retain wastes produced by the factory at the
test site. In so doing, a shunt for flow to the demonstra-
tion plant had to be provided. This new arrangement in-
creased the somewhat difficult problem of maintaining a
steady flow to the demonstration plant, and was followed
by a series of feed-pump failures. A survey of the problem
indicated that the modifications which had been made in the
main factory waste system led to the accumulation of weeds
and detritus near the feed-pump of the experimental ponds.
The series of pump failures that ensued was due mainly to
repeated clogging by weeds and detritus contained in the
factory wastes. These pumping problems made it impossible
to maintain continuous pumping in the modified system.
Inasmuch as waste input control had been a recurring problem,
and inasmuch as it apparently became an insurmountable prob-
lem under the budget and conditions existing in the fall of
1968, it was decided by the foundation that the experimental
Program should be abbreviated for lack of the possibility
of controlling the volume of waste input. Despite the fact
that the last experiments of 1968 involving the anaerobic-
algae pond in series were subjected to extremely close super-
vision and control, no steady-state could be obtained. In
retrospect after viewing the completed data, one realizes
that because of load variation, hopes for a high degree of
control were unrealistic. In fact, because of drastic chan-
ges in waste strength, no steady-state could have been attained
regardless of flow control, nor can one expect a true steady-
state to ever be maintained on the wastes of a beet sugar
factory.
OBSERVATIONS AND ANALYSES
In addition to measuring and maintaining records of pond
depth, detention period, recirculation, and mixing, the
studies also included measurement of air and water tempera-
tures and light energy input; as well as analyses to deter-
mine BOD, COD, total and volatile suspended and dissolved
solids, nitrogen, phosphorus, magnesium, calcium, sulfate,
and sulfide, algae and other organisms, and algae-packed
volume. Counts were made of coliform and fecal strepto-
cocci in the influent and at various stages in the system
during the previously reported runs in which the MPN dilu-
tion method was followed in estimating the concentration
of both groups. These results were presented previously
(2) and were not repeated in the later series.
14
-------
SAMPLING TECHNIQUES
Because of its variability, the waste flume water entering
the anaerobic pond was composited for analysis, A gravity
sampling line was installed to collect waste as it passed
through the influent parshall flume where volume was mea-
sured. The collected waste was conducted through the line
into a nearby refrigerated sample bottle located in a
refrigerator. The sample line passed through a solenoid
valve that was normally closed. By means of an interval
timer, the solenoid valve was opened each hour, permitting
about 1 quart of waste to flow to the sample bottle. The
contents of this bottle were designated as "influent" and
analyzed each day as typical of the influent waste to the
anaerobic pond.
During operation the anaerobic pond overflowed through a
control and metering weir either to the facultative pond
or to the algae pond, depending on the mode of operation.
Because of its long detention period (10 to 40 days) and
larger volume, the effluent from the anaerobic pond did
not vary rapidly in the quality from day to day. A grab
sample of the water passing over the weir was collected
daily at 9 A.M. and the contents of this sample was desig-
nated as "anaerobic" and analyzed each day as typical of the
effluent from the anaerobic pond.
During operation the facultative ponds overflowed through
a control and metering weir into the algae pond. Because
of its long detention period (10 to 40 days), the facultative
pond did not vary rapidly in quality. Accordingly, a grab
sample of the water passing over the weir was collected
daily when the pond was in operation and this grab sample
was designated as "facultative" and analyzed each day as
typical of the effluent from the facultative pond.
During the operation of the algae pond, it overflowed into
an effluent sump and into a recirculation sump. Because of
its long detention period (5 to 20 days) and large volume,
the effluent from the algae pond did not vary rapidly in
quality from day to day. It did, however, vary with time
of day, particularly with respect to pH, temperature and
dissolved oxygen. However, a 9 A.M. grab sample was collec-
ted daily and the contents labeled "algae". This was analyzed
each day as typical of the effluent from the algae pond.
Diurnal changes in the algae pond were detected when desired
by 24 hour sampling or by taking 3 P.M. samples in the pond
as well as the regular 9 A.M. samples.
15
-------
Inasmuch as the effluent sump and the recirculating sump were
located near one another in the algae pond, the sample labeled
"algae" was also assumed to be typical of the recirculant.
When, due to flow interruptions the ponds were not overflow-
ing, grab samples were taken from each pond near the outlet
where the overlfow samples would have normally been taken.
Although 24-hour compositing of all samples from each portion
of the system would have been desireable, budgetary limitations
and operational difficulties made such a sampling program
impossible. However, influent composite sampling was the
major need because influent variation was inherently far greater
than that of the effluents from the various ponds.
Routine analyses were made according to techniques given in
Volume 12 of Standard Methods for Examination of Water and
Wastewater (3}, with the exceptions described below.Gas
production was studied with Bronson gas collectors (shown in
Figure 4). Data on methane fermentation were limited to the
final series both because a clearcut methane fermentation
did not become established in the ponds, and because gas
emission measurements were interrupted by water condensation
in the transmission lines from the Bronson collectors to the
gas meters in all but the final runs.
FIGURE 4. BRONSON GAS COLLECTOR
16
-------
Instead of using the standard method test for odor in drink-
ing water, a method was developed for expressing odor, des-
cribed as the organoleptic test. This was done by establish-
ing six arbitrarily designated characteristic odors: 1 -
none; 2 - beets; 3 - other; 4 - cow dung; 5 - H2S; and 6 -
foul. Also, six intensities were arbitrarily established:
1 - being a very low intensity and 6 - being a high intensity.
The arbitrarily assigned numbers were multiplied together
to give an "odor product". The lowest odor product possible
is 1 and the highest, 36. A sample which smelled like H2S and
was moderately intense would have an odor product of 5 x 3
or 15. A strong beet smell would have a product of 2 x 6
or 12 and so on.
During November, 1968, because of apparent deficiencies in
certain nutrients in the main factory waste, a special bio-
assay was made to determine whether or not certain nutrients
such as potassium phosphate, ammonia phosphate, ammonium
nitrate, sodium nitrate, phosphoric acid (20%) , and 15-8-4
commercial fertilizer would be of any benefit to algae
growth and photosynthetic oxygenation in the system. The
bioassay technique used closely followed that for Provisional
Algal Assay Procedures recommended by the Federal Water
Quality Administration (4). Indigenous algae rather than
Selenastrum were used for the assay organism, and hand mixing
of the cultures was employed.
During the course of the studies, several 24-hour studies
were conducted to obtain information on the diurnal rates
of oxidation and photosynthesis in the ponds. Twenty-four-
hour studies of dissolved oxygen and temperature are extremely
valuable in systems undergoing oxidation and photosynthetic
oxygenation because the data permits an evaluation of the
rates of oxygen-use and the rates of oxygen production in the
system. One requirement for the success of such a 24-hour
study is the attainment of oxygen supersaturation at some
point in time. At the points in time that the dissolved
oxygen concentration of the pond is equal to the saturation
concentration for that temperature, no exchange of molecular
oxygen occurs with the atmosphere and consequently the observed
rates are independent of gas exchange, and are a function
solely of the difference between the rates of photosynthetic
oxygen production and respiration. In spite of several efforts,
supersaturation was reached in only one 24-hour study.
During the early summer of 1968, the algae pond system was
drained and modifications were made to prevent the short-
circuiting of flow under the baffles which had been observed
during the spring campaign. This short-circuiting was esti-
mated to have reduced the portion of the algae that was
17
-------
actually mixed to less than one-half the total area. Inas-
much as short-circuiting beneath the baffles caused this
problem, earth was piled on either side of the baffles to
about 12" above the base. It was found later that even this
drastic measure did not entirely prevent short-circuiting,
but it did reduce the short-circuiting considerably.
A schematic diagram of the system used for the final runs
is shown in Figure 5.
r-RECYCLE PUMPS
WASTE
_OW DIVIDER
r-SETTLING \
\V TANK \
F) T LTT
- Cy '*-L
T"-- DSM
T SCREEN
-£+-
7.
^EFFLUENT
PUMP
TO FACTORY PONDS AN-ANAEROBIC POND WITH
S HP AERATOR
R - RECIRCULANT
I - INFLUENT
T- TRANSFER
E- EFFLUENT
FIGURE 5. SCHEMATIC DIAGRAM OF SYSTEM AS APPLIED IN AERATED
ANAEROBIC PLUS MIXED ALGAE POND SERIES
The final run of the series was initiated on July 27, 1968,
and terminated on December 17, 1968. Desired operational
procedures for the final run were a feed rate of 150 gallons
per minute and a recirculation rate of 150 gallons per minute.
This rate was chosen on the theory that it would force more
of the BOD load to be conveyed through the anaerobic pond and
into the photosynthetic or algae pond. Nominal depths for the
ponds were to be 14' for the anaerobic pond; while the algae
pond was to have a variable depth beginning at 42" and adjus-
ted downward as light diminished.
Operating depths for the ponds during this period are shown
in Table 1. Every effort was expended to maintain the feed
at a constant rate but as noted previously, pump failures,
clogging, and extreme changes in waste concentration caused
both the hydraulic and organic feed rate to vary. In spite
of these difficulties, data collection was persistent and
complete, and the data were thoroughly processed to evaluate
major parameters.
18
-------
TABLE 1
Operating Depths for Ponds During July - Dec. 1968 Runs
Period
July
Sept
Nov.
- Aug.
. - Oct.
- Dec.
Nominal
Anaerobic
14
14
14
Operating Depth ft.*
Algal Pond
3.5
2.5
2.0
*Depths varied i several inches during
the course of each run.
All data gathered during the course of the entire study were
stored on IBM cards for subsequent processing. In machine
processing the data, mean values for the various stages of
the system were obtained as well as standard deviations and
variability. Correlations between a number of parameters
were sought and found. However, because of lack of funds,
complete processing of all possible combinations of all data
has not been possible. Accordingly, tabulations of all of
the day-to-day data from the final run are included in an
appendix to this report so that they can be further processed
by any who are interested and have the funds to do so.
19
-------
-------
SECTION V
RESULTS
GENERAL WASTE CHARACTERISTICS
One factor of considerable interest is that of the general
characteristics of beet sugar flume water. A compilation of
the mean values of all determinations made for the Holly
sugar waste during the 1965 to 1968 study is presented in
Table 2. Standard deviations for these values were very
large. As shown for the solids data in Table 2, the variance,
4/M, in some cases exceeded 1000%. Because of the great
differences, not all variances were computed, and hence the
blanks in Table 2.
PHOTOSYNTHESIS AND RESPIRATION
As noted previously, only one of the 24-hour studies under-
taken yielded data which could be used successfully in deter-
mination of respiration and photosynthetic rates . The pond
involved was the algae pond at a time when its nominal load-
ing was about 60 Ibs per acre per day. The run was made
before the baffles and mixing system were installed in the
algae pond.
Results of that run are plotted in Figure 6. From the figure
it may be observed that the exchange independent rate of res-
piration was 0.467 mg 02 per liter per hour, and the mean
photosynthetic rate at the surface netted 1.16 mg per liter
per hour. The gross surface photosynthetic rate including
respiration was 1.62 mg per liter per hour. From these data
the rate of oxygen-use by the pond was 86 Ibs per acre per
day. The net surface photosynthetic oxygen production was
214 Ibs per acre per day, and the gross surface rate, 300
Ibs per acre per day. Inasmuch as the rate decays logrith-
mically with depth, the average rate with depth would be about
one-third the surface rate or about 100 Ibs per acre per day.
The apparent photosynthetic efficiency of the algae pond,
assuming a sunlight energy input of 200 cal/cm2 per day,
was then about 2.3%. This rate of oxygenation is slightly
greater than the rate of deaeration based on the respiration
rate of the system. On the other hand, the respiration rate
of the system must have been more than satisfied because the
oxygen level was continuously near saturation. Inasmuch as
the system was supersaturated during daylight hours and barely
fell below saturation at night, there must have been a net
export of 02 from the system.
21
-------
TABLE 2
Mean Values for Certain Analytical Parameters of Holly-
Tracy Flume Water - 1965 - 1968
(Following 16 mesh DSM screening and 1*5 hr. sedimentation)
Parameter
Total Nitrogen (N)
Ammonia (N)
Nitrate (N)
Chlorides
Sulfate
Alkalinity (CaC03)
Sulfide
Phosphate (P)
Calcium
Magnesium
Sod ium
Potass lum
BOD (unfilt.)
COD (unfilt.)
COD (filt.)
Suspended Solids
Suspended Volatile
Suspended Ash
Dissolved Solids
Dissolved Volatile
Dissolved Ash
Total Solids
Total Volatile
Total Ash
Sugar
Dissolved Oxygen
Physical factors
PH
Light Penetration
Specific Conductance u mhos
Units
mg/1
H
II
II
It
It
tf
tl
tl
It
II
II
II
II
II
II
II
II
II
II
II
It
tt
It
II
II
cm
cm
Value
16.4
6.3
2.6
400 *
210.0
538.0***
0.68
3.4
178.0
66.0
222.0**
88.0**
930.0
1601.0
1195.0
1015
360
655
2209
1139
1070
3224
1499
1725
1.25
0.0
7.06
45.6
300
Variance
«
_.
--
fm
<
««
>
*
H
tfft
..
*!
..
11269
7140
6348
6016
2764
7754
14979
4456
8328
0.25
1.8
17.8
299
*Based on specific conductivity
**Single values
***By difference
22
-------
18
6
OBSERVED D.O,
RESPIRATION RATE
A0/flt= -0.467 mg///hr
\
MEAN PHOTOSYNTHETIC RATE
(NET) AO/At =+ 1.16 mg/^/hr
POND 3 , 3'DEPTH
3.1 ACRES, 2.834x10 gal.
I2N
4PM 8PM I2M 4AM
TIME - 20-2! APRIL 1967
8AM
I2N
FIGURE 6. DISSOLVED OXYGEN VS TIME OF DAY
FLOATING AERATOR STUDY
r
A five-horsepower floating surface aerator was installed in
the system on July 31, 1967 and was positioned in the anaero-
bic pond near the center as shown in Figure 1. During the
prior spring campaign, the anaerobic pond had been heavily
loaded; and following several weeks without feed, the BOD
remained at 325 mg per liter. Prior to the study, the odor
intensity level of the anaerobic pond was at the 10 to 12
level, and was characterized by a foul hydrogen sulfide stench
that had barely improved after standing several weeks. After
three days of aeration with the new aerator, the odor inten-
sity dropped to a level of 4. The odor quality became that
23
-------
characterized as "cow dung". By the seventh day, the odor
intensity level had dropped to 1.0, which was the lowest
value on the arbitrary scale used.
The COD and 5-day, 20°C BOD results for this aeration study
are shown graphically in Figure 7. In viewing these data,
it should be recalled that no feed was entering the anaero-
bic pond during the period August 1 to August 28, 1967; and
hence, the measurements simply indicate the rate of oxida-
tion of substances in the system resulting from aeration.
As is evident from Figure ,7, the BOD which was initially 330
mg per liter declined to 18 mg per liter on August 28; where-
as the COD steadily increased from 390 to 590 mg per liter
during the first four days, and then declined to 134 mg per
liter by August 28. The reason for the initial increase in
COD is unknown, but it was apparently due to the 5 HP surface
aerator bringing into suspension some material which exerted
a COD but not a BOD.
I 1 I I I I
5H.R Floating surface aerator
furnished by Welles Products
Corporation- Roscoe , Illinois
COD
BOD5
DISSOLVED OXYGEN
VILE ODORS GONE
13 15 17 19
AUGUST, 1967
FIGURE 7.
CHANGE IN COD, BOD AND D.O, IN ANAEROBIC POND DURING
SUSTAINED AERATION WITH 5 H.P. FLOATING SURFACE AERATOR
24
-------
During the period August 1 to August 16, no dissolved oxygen
was detected in the system. After August 19, dissolved oxy-
gen began to appear in the water during the afternoons,
although it would be at zero concentration in the mornings.
This indicates that after August 19 photosynthetic activity
was beginning to replenish oxygen in the system even while
oxygen was being introduced by the aerators.
During the period August 1 to August 16, the BOD decreased
from 335 mg per liter to 100 mg per liter. Thus, in 15 days,
the total reduction was 235 mg per liter. Inasmuch as during
this period the volume of the anaerobic pond was about 2.5
million gallons, the rate of oxidation must have been 235 x 2.5
x 8.34 = 4,900 Ibs of BOD or 327 Ibs per day. Assuming that
during this period natural reaeration contributed 20 Ibs per
day (the surface area being 1 acre), the aerator must have
contributed 307 Ibs per day or 2.54 Ibs per HP hr. This
rate is precisely that published by the manufacturer (5),
namely, 3.2 Ibs of $2 Per kw nr a^ zero dissolved oxygen.
The rate of change of COD was somewhat higher after the first
five days, but the overall rate, neglecting the initial "hump",
corresponds well with the change in BOD. The initial hump
probably resulted from the disturbance of bottom substances
which had a COD but little measurable BOD, It should be
noted that about 20 days were required to satisfy the pond
BOD and attain free molecular oxygen and that the odor level
had dropped to 1 when about one-third of the time had elapsed.
This corresponded to the satisfaction of about one-third of
the BOD.
During the period of mechanical aeration without loading, the
pH in the pond slowly decreased from 7.6 to 7.1 between August
1 to August 10, and then increased to 7.9 in the period August
11 to August 18. The increase probably was due to photosyn-
thetic activity.
ANAEROBIC WITH AERATION FOLLOWED BY FACULTATIVE POND
On August 28, 1967, the Holly sugar factory again began to
operate and produce wastes.
While construction of the mixing system for the aerobic pond
was in progress, the aerated anaerobic and facultative ponds
were operated in series. No recirculation was applied. Load-
ing to the anaerobic pond was at the rate of 25 gallons per
minute. The BOD of the influent ranged from 1308 to 1639 ppm.
The waste had a strong, foul odor, a brown color, and a nitro-
gen content of 64 mg per literindicating the intrusion of
Steffen waste into the flume water. The effluent BOD from the
anaerobic pond began to increase, and rose from 18 to 53 mg
25
-------
per liter within a week. It reached 129 mg per liter by
the end of the 25-gpm run. During the same time, the COD
rose from 134 to 228 mg per liter. Odor at first increased
and then declined. At the feed rate of 25 gallons per min-
ute, the organic load entering the anaerobic pond was between
400 and 500 Ibs per acre per day, exceeding by 75 to 175 Ibs
the daily aeration capacity of the 5 horsepower floating
aerator. Frequent interruptions in flow due to influent pump-
ing failures at first permitted the persistence of a small
residual of dissolved oxygen in the surface layers of the
anaerobic pond, and kept the odor intensity level down to
about 5. When the loading rate was increased to 50 gpm, all
dissolved oxygen disappeared from the system.
Key results of the 1967 fall runs 13 through 18 are summarized
in Table 3. According to the table, loadings varied from 900
to 0 Ibs per acre per day. Generally speaking, most of the
BOD was removed in the anaerobic pond.
Because of the high removals in the anaerobic pond, loadings
to the facultative pond were always less than 180 Ibs per
day. Effluents from the facultative pond varied from 45 to
140 mg per liter BOD, with little apparent relationship to
applied BOD. During this period, the facultative pond con-
tained a rich culture of Oscillatoria limosa which remained
in suspension, and apparently in some cases retained nitrogen
to the extent that nitrogen concentrations in the facultative
pond were higher than those in the anaerobic pond. 0. limosa
concentration in the facultative pond reached concentrations
approaching 100 mg per liter. Nitrogen concentrations in the
anaerobic pond were always less than those in the influent
a fact which confirms the high nitrogen removals in the anaero-
bic pond reported in the Third Progress Report (1).
ANAEROBIC WITH AERATION FOLLOWED BY ALGAE POND
Heavy rains from November through March of 1967-68 made pilot
plant operations impossible. The spring campaign at Holly was
initiated on March 28 and extended to May 27, 1968. The
anaerobic pond with aeration was operated in series with the
aerobic algae pond with mixing. The facultative pond was
bypassed. During the 60-day period, there were 10 days of
down time due to weather, and 44 days of down time due to feed
pump failures. Efforts were made to operate the system with
a feed rate of 100 gallons per minute, but again day-by-day
problems with pump clogging continuously interrupted the flow.
Various modifications were made in the waste transfer and feed
system, the major one being an automatic backflush cleaning
cycle installed on the feed pumps system. However, due to
large amounts of vegetation in the main factory waste, this
26
-------
TABLE 3
RESULTS
1967 Aerated Anaerobic Fond Plus Facultative Pond With No Keclrculation
Pond
Inf
An
Fac
Inf
An
Fac
Inf
An
Fac
Inf
An
Fac
Inf
An
Pac
Inf
An
Fac
Run
13
tt
ii
14
M
H
15
it
M
16
H
H
17
it
H
18
H
«
Flow
gal/min
25
50
75
0
50
50
Load
IDS
day
450
39
«
900
61
-.
900
180
mm
«
«
730
110
..
..
BOD
»g/l
1500
129
79
1490
101
77
983
200
113
726
314
140
1202
184
64
665
142
47
COD
rag/1
1776
321
370
1814
276
493
1532
402
512
«
452
550
1455
371
408
1220
402
426
Vol Sol
ng/1
1450
491
584
1172
401
625
781
412
631
454
454
508
1065
470
563
882
495
583
Total N
«g/l
22
15.2
20.5
38.9
17.7
24.3
23.2
20.4
23.6
15.7
21.7
35.0
21.4
20.7
25.8
25.2
21.6
Odor
product
12
5
3
16
9
3
6
10
3
6
10
3
4
14
3
""
«
27
-------
installation only slightly ameliorated the continual clogging.
Since recirculation rates of 100 gallons per minute (nominal)
were maintained throughout the period, a considerable amount
of the loading to the anaerobic pond was transferred forward
into the algae pond. In spite of flow interruptions, by
April 11, when a major pump failure occurred, the anaerobic
pond had begun to develop a sulfide odor and contained a
measured dissolved sulfide level of 0.5 mg per liter. During
this campaign, there was intermittent occurrence of daphnia
in the algae pond. The daphnia grazed the algae excessively.
As a result of the loss of algae through the grazing activity
of the daphnia, the dissolved oxygen dropped to near zero
on several occasions. When the major feed pump failure
occurred, a second feed pump was rushed into operation, but
was only installed a few days before factory shut down for
the summer break. Because of the sporadic nature of this
series and frequent interruptions due to weather and pump
failures, the data from this series of runs were not processed,
The final series of tests were conducted during the summer
and fall of 1968 (July 27 to December 18, 1968). As noted
previously, a great difficulty was encountered in maintaining
flow rates. Nevertheless, the experiments were conducted as
nearly as possible according to schedule and with detailed
recording of all factors. The results of this series of runs
are presented in more detail than were the others in an effort
to obtain maximum value from the study.
In order to simplify presentation of the data, daily values
for all parameters are tabulated in the Appendices as a
function of day and month. In some cases, seasonal varia-
tions' were predominant; but in most cases, day-to-day varia-
tions in the data were large. These variations probably
resulted mainly from genuine variations in the materials
sampled rather than from variations in the analytical tech-
niques, although the latter variations no doubt also occurred.
Machine processing of the data simply indicated the enormity
of the variations encountered and did little to clarify any
basic relationships. A number of strong relationships are,
however, quite evident from the data. Hence, the data to
be used in showing these relationships were reprocessed
simply by taking arithmetic averages of all data month by
month. Although this was a laborous and time-consuming pro-
cess, the results indicate that it was worthwhile. These
arithmetic averages are to be found at the bottom of each
column, of daily values in the Appendices. A statistical
treatment of the data was not made because its chronological
arrangement would have merely brought out variances due to
weather and changing waste characteristics which are quite
obvious in the daily data. In addition to being presented
in the Appendices, groups of arithmetic means which may lead
28
-------
to conclusions are also presented in tabular form in the
body of the report and are plotted in figures where greater
clarity is required for discussion.
ENVIRONMENTAL CONDITIONS - Results of daily measurements of
solar energy waste and pond temperatures, and maximum and
minimum air temperatures are tabulated in Appendices A-l,
A-2 and A-3. Monthly mean values for each of these para-
meters are plotted in Figure 8.
350
UJ
cc
:D
-------
As indicated in the figure, visible solar energy varied from
a mean of about 225 gm cal per cm^ in August to a mean of
about 50 gm calories per cm^ in December.
Mean monthly maximum air temperature declined from 37°C in
August to 12°C in December, and the mean monthly minimum
air temperature dropped from 17°C in August to 1°C in Decem-
ber.
During the series, the monthly mean waste temperature dropped
from a maximum of 34.4°C in August to a minimum of 27.7°C
in December. In spite of the large amount of heat conveyed
into the anaerobic pond by way of the warm factory waste,
the temperature of the pond varied from a monthly mean of
22.2°C in August to 11.0°C in December. The algae pond varied
from 21°C in August to 9.6°C in December.
During the winter the mean temperature of an open pond tends
to be equal to the 24-hour mean air temperature. According
to the observations recorded in Appendix A-3, however, pond
temperatures were higher than normal during the cooler months
of October, November, and December; and somewhat lower than
the mean air temperature in August and September. The indi-
cation is that due to recycling, some waste warmth was retained
and carried forward even into the algae pond during the cold
months; and that both the algae pond and the mixing that
occurred in the anaerobic pond brought about by the surface
aerator had a substantial cooling effect upon the waste mass
due to evaporation during the warmer months. The constant
difference of about 1.5°C between the anaerobic and algae
pond during the entire period is evidence of the effective-
ness of recycling as a mixing mechanism. In this system,
when there was incoming waste, recycled water was mixed with
the incoming waste. Inasmuch as this mixture was normally
much warmer than the pond water, it found its place at the
surface of the anaerobic pond where it was subject to mechani-
cal aeration and evaporative cooling. On the other hand,
when the feed pump was clogged, the recycled water entering
the anaerobic pond was on the average cooler than the contents
of the anaerobic pond, and hence, probably found its way to
the bottom of the pond. Since the recirculated water often
contained oxygen, its presence at the bottom of the anaerobic
pond would have had an inhibitive effect upon methane fer-
mentation.
FLOWS - Daily data for the four waste streams "influent",
"recirculant", "transfer", and "effluent" are presented in
detail in Appendices B-l, B-2 and B-3. The meaning of the
term I, influent, R, recirculant, T, transfer, and E, effluent
as applied to the waste streams can be visualized through
30
-------
reference to Figure 5 in which each stream is indicated by
an arrow labeled with the appropriate letter.
As noted previously and as is evident from the data, the
steady-state conditions were never approached in the system.
Plow interruptions due to pump clogging and pump failure
frequently occurred for reasons previously described.
Variability in the feed stream plus variations in percola-
tion and evaporation led to loss of volume, so that the volume
of effluent should have theoretically always been less than
that of the influent. However, as indicated in the summary
table for flows, cf. Table 4, mean effluent flow in September
exceeded the influent flow. This reflected the fact that
the algae pond initially was to be filled to about 42". Dur-
ing August it became evident that this depth was excessive
and a depth of 30" was determined to be more favorable. Inas-
much as the pond already had been filled to a depth of about
41", some 600,000 gallons of excess water had to be discharged,
During November, another apparent anomaly occurred in which
effluent exceeded influent. In this case, interruptions in
the influent flow reduced the mean influent to 17 gpm while
rainfall plus a second depth adjustment of the algae pond to
a nominal depth of 24" increased the mean effluent to 33
gallons per minute. Nominal operational depths for the ponds
during the various periods were shown previously in Table 1.
The longest sustained run was made during October, a month
in which evaporation is normally equal to precipitation.
Because evaporation equalled precipitation, the difference
of 52 gallons per minute between influent and effluent was
due mainly to percolation. This difference amounted to about
75,000 gallons per day or 19,000 gallons per acre per day
over the ponding area. This rate is somewhat higher than is
generally reported for ponds in the Tracy area and may reflect
errors in flow measurement.
LOADINGS - Because of wide variations in flows and BOD values,
only crude materials balances could be established for the
system. Measures of unfiltered COD, filtered COD, and unfil-
tered BOD were made frequently on the influent and on the
effluent from the anaerobic and algae ponds. All of these
data are tabulated in Appendices C-l, C-2 and C-3, and the
monthly mean values are summarized in Table 5. According
to Table 5, the unfiltered COD of the factory waste increased
from a mean value of 1482 mg per liter in July to a mean
value of 2380 mg per liter in December. The corresponding
filtered COD values increased from a mean of 603 mg per liter
in July to 1969 mg per liter in December. Thus, the increase
in COD during the course of the campaign apparently was due
to the presence of soluble substances. The unfiltered BOD
31
-------
TABLE 4
Summary of Mean Monthly Flow Values for Influent
Recycle, Transfer and Effluent Waste Streams
Month
Jul
Aug
Sept
Oct
Nov
Dec
Stream
Influent1
Recycle1
Transfer
Effluent1
I
R
I
E
I
R
T
E
I
R
T
E
I
R
T
E
I
R
T
E
Monthly Mean Flows
Gal/Min
61
148
* ** .
105
148
100
22
75
148
183
902
128
148
195
76
17
23
26
333
82
82
113
36
CUl{dgr
88.0
216
*
152
215
144
32.0
108
215
264
1302
185
215
282
110
24.5
33.1
37.4.
47. 53
118
118
163
52.0
For significance of terminology see Figure 5
2Effluent exceeded influent due to draw down of
algal pond to reduce operating depth from 40" to 30"
Effluent exceeded influent because of rainfall* depth
reduction and reduced influent
32
-------
TABUS 5
Summary of Monthly Mean COD and BOD Values
as a Function of Pond and Month
Month
Jul1
Aug
Sept
Oct
Nov
Dec
Samp
Inf
An
Al
Inf
An
Al
Inf
An
Al
Inf
An
Al
Inf
An
Al
Inf
An
Al
Unfilt
COD
mg/1
1482
261
150
1450
389
314
1559
630
544
1570
750
656
1960
715
610
2380
759
579
Filt
COD
mg/1
603
119
142
961
217
112
1128
144
116
1180
137
104
1541
209
150
1969
165
130
COO
BOD
Unfilt
1.85
2.54
3.00
1.48
2.11
3.20
1.81
3.78
4.17
2.50
8.25
11.90
2.01
6.0
11.0
2.47
9.80
10.00
Unfiltered BOD
5-day 20°C
mg/1
803
103
50
985
184
98
863
167
130
625
91
56
971
119
55
963
78
58
Ult 20°C
mg/1
1180
151
73
1440
269
143
1260
245
191
915
133
82
1420
174
81
1410
114
85
Ult 20°C
lbs/1000 gal
9.85
1.61
0.61
12.00
2.24
1.19
10.50
2.04
1.59
7.60
1.11
0.68
11.80
1.45
0.67
11.75
0.95
0.70
Filt
BOD
mg/1
132
103
Values for July are based on single or duplicate tests only
2Single sample
3Mean of four weekly samples
33
-------
did not parallel the COD, but rather decreased in October.
This decline raises the definite possibility of the presence
of toxic or refractory substances in the pond or waste dur-
ing October, November, and December, inasmuch as the normal
COD-BOD ratio for raw waste has been found to be about 1.67
(1), and for completely treated waste, on the order of 4.
These ratios do not account for changes in solubility of
organics, for their refractory characteristics, or for their
toxicity. A further description of the results of the BOD
and COD studies will be presented in a later section. For
the present, only loading and overall system performance are
given.
Unfiltered BOD values were used together with flow data to
compute loadings. The unfiltered 5-day, 20°C BOD values are
plotted in Figure 9. Monthly mean loadings and performance
data based upon monthly mean flows and BOD values (converted
to ultimate BOD) for the anaerobic-algae pond in series are
listed in Table 6. A study of the table shows that with
the exception of September and November, when depth adjust-
ments were made, the system attained a 95% or better overall
ultimate BOD removal, and that even though a large amount of
waste water was discharged in September, an overall removal
of 84% was attained. The input-output balance for the two
ponds shows that little or no net removal was attained in
the algae pond in that the amount varied from -3 to 30 Ibs
per acre per day. The major removals in the system were
attained in the anaerobic pond. The algae pond did, however,
convert some of the BOD to a more removable form, as is evi-
denced by the fact that the filtered BOD from the algae pond
was as low as 10 mg per liter. Had complete separation of
the solid fraction from the algae pond effluent been a routine
procedure, the overall BOD removal of the system referred to
as soluble BOD would have been in excess of 99%. It should
be noted that one of the major factors contributing to poor
overall BOD removals in the algae pond in terms of unfiltered
algae pond effluent was the fact that it was continuously
mixed. Another factor was the presence of predators in the
pond which occasionally destroyed the algae crop almost en-
tirely, and thereby reduced the pond dissolved oxygen to zero.
Another contributing factor was that inasmuch as the anaero-
bic pond was so efficient, the applied loading to the algae
pond was low, the opportunity for removal was also low.
In general, BOD removal in the anaerobic pond was found to be
directly proportional to loading at all loading rates up to
2,000 Ibs per day. The concentration of ultimate BOD moving
into the algae pond was greater than 245 mg per liter in
August and September and over 114 mg per liter in October,
November, and December. BOD values of this magnitude are
not normally acceptable in the aquatic environment, hence,
34
-------
although the anaerobic pond accepted high loadings and
accomplished high removals, it often was malodorous and
discharged an effluent having a high BOD. Thus, even though
the algae pond was apparently inefficient, it was an essen-
tial part of the system because it brought about a decrease
in the final BOD of the overall system to a level which^would
be acceptable in the aquatic environment, particularly if the
algae were removed.
1400
1200 h-
1000
£
Q" 800
til
CD
£600
O
400
200 \
UNFILTERED BOD 5 DAY 20°C VALUES
INFLUENT
A-- ANAEROBIC
D ALGAE
A'
D-
a-
.-D
JUL
AUG
SEP OCT
MONTH
NOV
DEC
FIGURE 9. MONTHLY MEAN VALUES^FOR UNFILTERED BOD AS A
FUNCTION OF POND AND MONTH
35
-------
TABLE 6
Monthly Mean Flows BOD Values and Performance Data for
Anaerobic-Algae Pond in Series
Month 1967
I* Flow GPM (mean)
BOD of I mg/1 (mean)
I Load Ibs/day
Ibs/acre/day
R* Flow GPM (mean)
BOD of R mg/1 (mean)
R Load Ibs
An* Load Ibs/day
influent + recycle
T* Flow GPM (mean)
BOD of T mg/1 (mean)
Al* Load Ibs/day
Ibs/acre/day
An Removal Ibs/day
E* Flow GPM (mean)
BOD of E mg/1 (mean)
Load Dlsch Ibs/day
E * R Ibs/day
Al Rem Ibs/day
Ibs/acre/day
BO) Rem Eff An %
BOD Rem Eff Al %
Overall Eff % of
BOD Removal
Jul
88
1180
870
n
--
73
..
151
,.
73
»
<<
«
...
Aug
IDS
1440
1810
tt
148
142
255
2060
100
268
322
107
1738
22
142
38
293
29
10
95.5
9.0
98
Sep
75
1260
1134
it
148
191
341
1475
183
245
538
179
937
90
191
207
548
-10
- 3
64
-1.8
84
Oct
128
915
1406
w
148
82
147
1553
195
133
313
104
1240
76
82
75
222
91
30
80
29
95
Nov
17
1420
290
it
23
81
22
312
26
176
54
18
258
33
81
32
54
00
00
83
00
89
Dec
82
1410
1380
n
82
85
83
1463
113
114
156
52
1307
36
85
37
120
36
12
89
23
98
* Letters identified in Figure 5
N.B. All BOD values are ultimate BOD's, i.e. 5-day BOD/.684
36
-------
The magnitude of decrease in BOD in the algae pond was from
30 to 126 mg per liter. It apparently also rendered the
recirculant more treatable in the sense that additional sub-
stantial removals were attained as recirculated waters were
again passed through the anaerobic pond.
PHYSICAL CHARACTERISTICS OF LIQUIDS - Physical characteris-
tics of influent and anaerobic and algae pond effluents are
tabulated by day and month in Appendix D. Included are pH,
(D-l), dissolved oxygen (D-2), volatile and fixed dissolved
and suspended solids (D-3, D-4, D-5, D-6), centrifuged volu-
metric solids (D-7), conductivity (D-8), and light penetra-
tion (D-9).
pH: A summary of pH relationships for the period is given
in Figure 10. In general, influent pH variations were ex-
tremely large, varying from 5.8 to 11.7 throughout the period.
The middle value as evidenced by the horizontal line in the
vertical bars of Figure 10 was about 8.6 in August, 7.6 in
September, 9.1 in October, 8.8 in November, and 8.5 in Decem-
ber. By contrast, the pH in the anaerobic pond varied a
maximum of 2.0 units, and in most cases was 1 full unit lower
than that of the influent. Its level was 7.55 in August, 7,75
in September, 8.1 in October, 7.7 in November, and 6.5 in
December. The low value in December possibly indicates that
due to low temperatures, a buildup of volatile acids was
occurring in the system at that time. The high value in
October perhaps indicates restricted biological oxidation
and C02 production.
When photosynthetic activity occurs in a pond, the pH usually
tends to increase particularly as a function of time of day.
This in turn leads to an overall increase in pH throughout a
pond system. The degree of increase in pH in the algae pond
during August and December was not large; and in fact was
found to have decreased in September, October, and November.
As will be demonstrated later, a severe rotifer infestation
occurred in the ponds during the last-named three months.
In spite of the evident decreases in pH from the anaerobic
to algae pond, a detailed perusal of the data in Appendix
D-l will show that in many cases there was indeed an increase
in pH. Considerable photosynthetic activity also took place
in the anaerobic pond, as was shown by the algae concentra-
tion of the pond.
Dissolved oxygen is, of course, one of the major indicators
of photosynthetic activity and this was measured twice daily
in the influent, anaerobic and algae ponds. It was found
that free molecular oxygen never was present in the influent,
and that the free molecular oxygen in the anaerobic pond was
37
-------
10
X
o.
KEY
tfl
FEED ANAEROBIC AL6AE
POND POND
AU6
SEP
OCT
MONTH
NOV
DEC
FIGURE 10.
EXTREMES AND CENTRAL TENDENCY pH RELATIONSHIP
IN INFLUENT, ANAEROBIC AND ALGAE POND AS A
FUNCTION OF MONTH
always zero after loading was first applied. Thus, the aera-
tion capability of 307 Ibs per day of the floating aerator plus
normal reaeration was quickly overwhelmed by the load rate.
Also, after about one week of loading and recirculation, the
38
-------
algae pond became devoid of dissolved oxygen during the morn-
ing sampling period. Thus, the only data reported in Appen-
dix D-2 are for 3 PM dissolved oxygen in the algae pond.
These data are presented graphically in Figure 11.
ib
14
12
^
o>
E
. *
-------
As is evident from the figure, beginning with high values
in July, the DO Values varied from 0 to 15.9 mg per liter
in August with a mean of 3,5 mg per liter; from 0 to 13.6
mg per liter in September with a mean of 3.1 mg per liter;
from 0 to 8.8 mg per liter in October, with a mean of 2.0
mg per liter; from 2 to 14 mg per liter in November, with
a mean of 8.4 mg per liter; and from 0 to 13 mg per liter
in December, with a mean of 4.6. The low-PM dissolved oxy-
gen concentrations observed during several periods resulted
from heavy loadings and from the destruction of algae by
predators. The high November means accompanied the drasti-
cally decreased loadings which occurred when the feed pump
failed.
The fact that dissolved oxygen always declined to zero in
the algae pond during the night and often remained near
zero all day indicates that the waste going to the algae
pond, as well as the contents of the algae pond were not
fully stabilized. This is also indicated by the relatively
high COD and BOD values found for the algae pond, particularly
during August and September when predators were most active.
The mean five-day BOD concentrations of 56, 55 and 58 mg per
liter in the algae pond during October, November and December,
while being spectacularly low as compared with those of the
influents at that time, actually represent unstable cellular
(suspended) material which were carried in the mixing system
and would place an additional load on a receiving body if
discharged. If this material were separated, the filtered
supernatant would have a BOD of only 10 to 20 mg per liter,
indicating that little residual soluble BOD remained. The
small amount that would remain should cause very little dis-
solved oxygen depression in a receiving stream. Another
problem pertaining to dissolved oxygen in the algae pond was
that the transfer of reduced sulfides from the anaerobic pond
into the algae pond placed an additional demand upon the
limited supply of dissolved oxygen. The magnitude of this
problem will become evident in the presentation of results
on sulphur transformations.
Solidsi As noted previously, the concentrations of the dis-
solved and of the suspended solids of the various samples
were determined, as were the respective ash (fixed) and vola-
tile concentrations of these fractions. A complete tabu-
lation of the daily ash (fixed) and volatile solids content
of the dissolved and suspended solids in each pond component
and month is presented in Appendices D-3, D-4, D-5 and D-6,
and the monthly mean values are summarized in Table 7.
A plot of volatile dissolved solids concentrations from Table
7 as a function of pond and month is shown in Figure 12.
40
-------
TABLE 7
Summary of Solids Data
Monthly Mean Dissolved Solids mg Per Liter
Month
Jul
Aug
Sep
Oct
Nov
Dec
Volatile
In
975
1358
1150
1250
1513
2142
An
333
520
477
608
557
606
Al
268
391
441
528
507
523
Ash
In
1039
1128
1118
946
1215
1129
An
1164
1002
922
831
898
884
Al
1149
1099
978
930
935
954
Total
In
2014
2486
2268
2196
2728
3271
An
1497
1522
1399
1439
1455
1490
Al
1417
1490
1419
1458
1442
1477
Monthly Mean Suspended Solids mg Per Liter
Month
Jul
Aug
Sep
Oct
Nov
Dec
Volatile
In
105
241
378
199
199
327
An
84
128
376
452
413
492
Al
94
156
374
414
369
395
Ash
In
148
239
465
447
212
472
An
19
25
82
155
79
152
Al
20
27
88
131
75
98
Total
In
253
480
843
646
411
799
An
103
153
458
607
492
644
Al
114
183
462
545
444
493
Monthly Mean Total Solids mg Per Liter
Jul
Aug
Sep
Oct
Nov
Dec
Volatile
In
1080
1599
1528
1449
1712
2469
An
417
648
853
1060
970
1098
Al
362
547
815
942
876
918
Ash
In
1187
1367
1583
1393
1427
1611
An
1183
1027
1004
986
977
1036
Al
1169
1126
1066
1061
1010
1052
Total
In
2267
2966
3111
2842
3139
4070
An
1600
1675
1857
2046
1947
2134
Al
1531
1673
1881
2003
1886
1970
41
-------
24
20 -
^
e
QC
UJ
LiJ
o
o
UJ
o
en
to
o
16
12 -
SUSPENDED MATERIAL REMOVED BY FILTRATION
0- INFLUENT
A ANAEROBIC
Q ALGAE
in Ax .--
to a-"
(I) SINGLE VALUES
I
JUL
AU6
SEP OCT
MONTH
NOV
DEC
FIGURE 12. MONTHLY MEAN DISSOLVED VOLATILE SOLIDS AS A
FUNCTION OF POND AND MONTH
Dissolved volatile solids in the influent varied from 975
mg per liter in July to a mean of 2142 mg per liter in
December. This increase in soluble volatile matter probably
resulted from a deterioration in beet quality with release of
putrescible materials. A similar but even more pronounced
increase in solubles was also observed in the filtered COD
of the influent discussed previously. Influent dissolved
volatiles were decreased by more than 60% in the anaerobic
pond, and by an additional approximately 10% in the algae
pond. During November and December, the reduction in dissolved
42
-------
volatile solids exceeded 70%, indicating that the soluble
fraction was not only greater in magnitude than the insoluble
but was also more readily decomposed.
A plot of the dissolved ash is shown in Figure 13. The
influent dissolved ash had a mean value of 1096 mg per liter,
and with the exception of the October mean, all values were
within + 10% of this value. The October value was minus
about 15%. A definite downward trend is evident in the
dissolved ash concentration in the anaerobic pond and in the
algae pond, indicating a precipitation of some relatively
heavy material. The drop was greater in the anaerobic pond
than in the algae pond, indicating that a degree of recon-
centration, perhaps due to evaporation, occurred in the algae
pond.
1400
12 OO
1000
. 80O
400 -
200
SUSPENDED MATERIAL REMOVED BY FILTRATION
A-
D-
INFLUENT
ANAEROBIC
ALGAE
JUL
AUG
SEP OCT
MONTH
NOV
DEC
FIGURE 13. MONTHLY MEAN DISSOLVED ASH AS A FUNCTION OF
POND AND MONTH
43
-------
A plot of suspended volatile solids is shown in Figure 14.
While the mean influent suspended volatile concentrations
were quite erratic, they were generally significantly
less than those in the anaerobic and algae pond. The build-
up of suspended volatiles in both the anaerobic and algae
pond was at a rate typified by a growth curve. The greatest
concentration of suspended volatiles occurred in the anaero-
bic pond in December. As would be expected, an examination
of the packed centrifuged solids (cf. Appendix D-7 and Figure
15} indicated that this suspended material was primarily
bacterial in nature in the anaerobic pond, and primarily
algae material in the algae pond. It is interesting to note
that the overall packed volume was greatest in the algae
pond, indicating that the suspended solids in both the in-
fluent and anaerobic pond were mainly finally divided or
colloidal, and hence not removable by centrifuging at 500
x gravity for 10 minutes. This supports the idea that the
material was primarily colloidal or very fine.
SUSPENDED MATERIAL REMOVED BY FILTRATION
, 400
H 300
-------
3.0
2.0
§
en
o
o
in
CO
9
O
en
O
cs
£
UJ
O
tu
O
y i.o -
O
o
UJ
o
D
INFLUENT
A-- ANAEROBIC
n ALGAE
AUG
SEP
OCT
MONTH
NOV
DEC
FIGURE is.
MONTHLY MEAN PACKED VOLUME OF CENTRIFUGED
SOLIDS AS A FUNCTION OF POND AND MONTH
A plot of the monthly mean suspended ash in the influent
and two ponds is shown in Figure 16. As is evident from
fcttiS figure, the concentration of suspended ash in the
influent was much higher than that in the pond suspended
material ranging from 50% to 69% in the influent, from
16.0% to 25.4% in the anaerobic pond, and from 14.8 to
45
-------
24.0% in the algae pond. The corresponding mean ash contents
were 57%, 19.6%, and 18.7% respectively. The indication is
that less than half of the suspended material in the influent
was organic; whereas the material in the anaerobic and algae
ponds had ash contents of a magnitude normally associated
with microbial cellular material. Thus, this is additional
evidence that the colloidal material in the anaerobic pond
was mainly bacterial cellular material; while that in the
algae pond was primarily algae material. There was, however,
substantial amounts of algae material in the anaerobic pond,
and of bacterial material in the algae pond due to the high
rate of recirculation and mixing.
600
E 400
I
01
<
o
UJ
o
z
UJ
Q.
tn
u
en
200
SUSPENDED MATERIAL REMOVED BY FILTRATION
0 INFLUENT
--A ANAEROBIC
U ALGAE
JUL
AUQ
SEP OCT
MONTH
NOV
DEC
FIGURE 16. MONTHLY MEAN SUSPENDED ASH AS A FUNCTION OF
POND AND MONTH
46
-------
Conductivity: Daily and monthly mean values for conductivity
are shown in Appendix D-8 and means are plotted in Figure 17.
Although the influent conductivity varied, it oscillated
around a mean value of about 310 micro mhos, whereas the
conductivity of the algae pond and the anaerobic pond stead-
ily increased throughout the run period. At first glance
this could be attributed to a simple salt concentration fac-
tor due to evaportaion; but a comparison of the monthly mean
dissolved ash and the monthly mean conductivity of the three
Sampling points indicates that there was a substantial change
in the physical nature of the solids in the ponds. Thus, in
the algae pond and in the anaerobic pond, a smaller quantity
of dissolved ash was associated with higher specific conduc-
tance than was true in the influent. This effect was slightly
more pronounced in the anaerobic poi.d than in the algae pond.
b 200
(I) SINGLE VALUES
O INFLUENT
A~_ ANAEROBIC
O ALGAE
SEP OCT
MONTH
FIGURE 17. MONTHLY MEAN CONDUCTIVITY AS A FUNCTION OF POND
AND MONTH
47
-------
Light Penetration; Values found in measurements of light
penetration through the influent and pond contents are tabu-
lated in Appendix D-9 and the monthly mean values are plotted
in Figure 18. As is indicated in the figure, following a
month of operation, light transmission was greatest in the
influent and least in the anaerobic pond. Intermediate
transmittance was attained in the algae pond. Both complexed
sulfides and algae strongly absorb light. Algae and sulfides
occurred in the anaerobic pond and light absorption was due
to both. Inasmuch as algae constituted the major portion of
suspended solids in the algae pond, light absorption was
mainly by algae when oxygen was present. When dissolved
oxygen was very low, turbidity from metal sulfides absorbed
much of the light. Also, inasmuch as the pond was mixed,
some of the light absorption probably was due to clay tur-
bidity induced by the mixing velocity of about one foot per
second. Inasmuch as light penetrated only about 30 centi-
meters into the algae pond, about two-thirds of its approxi-
mately three-foot depth was in darkness even during the day.
Photosynthesis then could only contribute oxygen in the top
foot of the pond.
Chemical Changes: The major ions studied were magnesium,
calcium, and sulfate. Sodium, chloride,and alkalinity deter-
minations were not made routinely although retrospectively
it is felt that they should have been made so as to permit
a complete evaluation of chemical transformations in the
System.
Daily values together with monthly mean values for magnesium
are tabulated in Appendix E-l and are presented in graphic
form in Figure 19. An examination of the figure indicates
that magnesium inputs into the system varied from about 40
to about 75 mg per liter. The peak occurred in October and
the minimum in December. There is little evidence of a sys-
tematic change in magnesium in the anaerobic pond with respect
to time. If compared with the anaerobic pond, the plot for
the algae pond does, however, indicate a systematic change.
Beginning in August with a mean monthly value of 10 mg per
liter greater than that of the anaerobic pond, it declined
to values about equal to that of the anaerobic pond in Sep-
tember; to 5 mg per liter less in October; to 15 mg per liter
less in November; and to about 11 mg per liter less in
December. These values are much more than one would expect
for biological uptake. They indicate that magnesium was
undergoing a precipitation with some type of anion in the
algae pond.
48
-------
it*.
vo
MONTH
FIGURE 18.
MONTHLY MEAN LIGHT PENETRA-
TION AS A FUNCTION OF POND
AND MONTH
0) SINGLE VALUES
(2 FOUR VALUES
-O INFLUENT
-A ANAEROBIC
-D ALGAE
JUL flUG
SEP OCT
MONTH
FIGURE 19. MONTHLY MEAN MAGNESIUM
CONCENTRATION AS A FUNCTION
OF POND AND MONTH
-------
Mean monthly calcium values are presented in detail in Appen-
dix E-2 and are plotted in Figure 20. Following an initial
low value for calcium in the ponds and in the feed in late
July, there was a 100 mg per liter increase of calcium in the
feed. This apparently declined somewhat with respect to time
thereafter. The October decrease in calcium is countered by
a similar increase in magnesium. Inasmuch as these two chemi-
cals are determined by manipulation of the same samples, this
relation could indicate a systematic experimental, analytical
or calculation error during the October period. This even-
tually is further supported by the fact that only four mag-
nesium determinations were made during the last week of Octo-
ber due to a temporary lack of the chemical Univer used in
the magnesium analysis. This lack was due to failure of a
supplier to fill an order on time.
-A
-n
INFLUENT
ANAEROBIC
ALGAE
(I) SINGLE VALUE
(2) FOUR VALUES
SEP OCT
MONTH
FIGURE 20. MONTHLY MEAN CALCIUM CONCENTRATION AS A
FUNCTION OF POND AND MONTH
50
-------
In spite of these difficulties, the evidence is clear that
a decrease in calcium occurred following the introduction
of the waste into the anaerobic pond. The magnitude of the
change involved about 50% of the influent calcium. This
probably was due to precipitation and sedimentation of sus-
pended colloidal calcium. Apparently no systematic increase
or decrease of calcium took place in the transfer from the
anaerobic pond to the algae pond, as was the case with mag-
nesium. Thus, the evidence is that calcium decreased most
substantially in the anaerobic pond, and magnesium decreased
most substantially in the algae pond. With respect to the
microbial and algae nutrition aspect of the problem, it is
evident that both calcium and magnesium were present in vast
excess.
The cation ammonium was systematically studied in these experi-
ments. Results pertaining to it are presented in the dis-
cussions of the other nutrients. The only major anion sys-
tematically studied was sulfate. The minor anions nitrate
and phosphate also were studied. These results are also
presented in conjunction with those for other nutrients.
Daily and monthly mean values for sulfate are tabulated in
Appendix E-3, and monthly mean values are plotted as a
function of pond and month in Figure 21.
An examination of Figure 21 indicates that during the course
of the experiments, influent sulfate concentration rose
slightly during August and September (from 215 to 265 mg per
liter), and then declined from September through December
(from about 250 to about 150 mg per liter). In the anaero-
bic pond a steady decline in sulfate took place from an
initial level of about 120 mg per liter in July to about 60
mg per liter in September. In the period from September to
December, sulfate in the anaerobic pond increased slightly
(about 10 mg per liter). A sulfate removal in excess of 50%
was effected in the anaerobic pond.
Sulfate concentration in the algae pond ranged from 10 to
35 mg per liter greater than that in the anaerobic pond, the
mean increasing being about 25 mg per liter. The presence of
more oxidized sulfur in the algae pond than in the anaerobic
pond indicates that sulfate was first reduced in the anaerobic
pond to sulfides and then oxidized to sulfate in the algae
pond. This, of course, indicates that insoluble sulfides
moved from the anaerobic pond into the algae pond in sub-
stantial quantities. The form in which these sulfides moved
is of some interest and will be discussed later.
51
-------
--A
INFLUENT
ANAEROBIC
ALGAE
(I) D-
\
X
D-.
\
X
A-
(I) SINGLE VALUE ONLY
SEP OCT
MONTH
FIGURE 21.
MONTHLY MEAN VALUES FOR SULFATE AS A FUNCTION
OF POND AND MONTH
According to the available data, it would also be informa-
tive to relate sulfate reduction to temperature. In Figure
22, monthly mean sulfate reduction is plotted as a function
of monthly mean temperature in the anaerobic pond. As shown
in the figure, the sulfate reduction is a linear function of
temperature between 10 and 25°C, the relationship being
R% = 55 + 2 (T - 10) (1)
This relationship did not hold in August when the ponds were
first started, but it did hold during September, October,
November, and December. The dotted line in Figure 22 indi-
cates the probable .general relationship between temperature
and sulfate reduction, but the data are insufficient,to sup-
port or disprove this hypothetical relationship.
52
-------
10 15 30
WATER TEMPERATURE,°C
FIGURE 22.
SULFATE REDUCTION IN ANAEROBIC POND AS A
FUNCTION OF TEMPERATURE
Other factors related to sulfate reduction are presented
in the section "Discussion".
Daily and monthly mean sulfide determinations for the period
August through December for the influent and the two ponds
are presented in Appendix E-4 and a plot of the monthly mean
values is presented in Figure 23. As shown in the figure,
daily values for soluble sulfides were initially quite high.
Some concentrations in the anerobic pond were found to be
as much as 6 mg per liter during August. These concentra-
tions decreased rapidly as the loading progressed, indicating
that those sulfides produced from sulfate reduction were
53
-------
2.0
1.5
0,5
D
|
- INFLUENT
- ANAEROBIC
AEROBIC
AUG
SEP
OCT
MONTH
NOV
DEC
FIGURE 23.
MONTHLY MEAN DISSOLVED SULFIDES AS A FUNCTION OF
MONTH
rapidly complexed or combined with some substance contributed
by the applied waste. A regression analysis of the daily sul-
fide and magnesium values indicates a correlation of +88%
between the two; whereas correlations between other factors
were much lower. Thus, it is believed likely that the form
in which the sulfides were carried from the anaerobic pond
to the algae pond was in the form of insoluble but suspended
magnesium sulfide. Once in the algae pond where oxygen was
54
-------
frequently in excess, this material probably was oxidized to
magnesium sulfate. Inasmuch as magnesium sulfate is soluble,
the magnesium would then be free to interact with other anions
to produce less soluble complexes such as magnesium hydroxide
and thereby lead to the slight reduction in magnesium in the
algae pond noted in the magnesium results presented previously
The increase in sulfides from influent to the anaerobic pond
shown in Figure 23 is to be expected in view of the sulfate
reduction depicted in Figure 21. An absence or low level of
sulfides in the algae pond is evidenced in the figure and is
to be expected in view of the generally aerobic environment
of the algae pond.
Through a comparison of the monthly mean dissolved sulfides
in the system with the BOD removal in the system as set forth
in Table 6, an apparent relationship between loading and dis-
solved sulfides becomes apparent. The relationship is plotted
in Figure 24. According to the figure, with the exception of
concentrations observed during November during which loading
was interrupted and sporadic, dissolved sulfides concentra-
tions were inversely proportional to the loading, attaining
a maximum in August when the loading was at its maximum. The
dotted line indicates a hypothetical relationship between
loading and soluble sulfides as suggested by the data. The
indication is that loadings above 1,000 Ibs per acre per day
will be accompanied by increasing quantities of dissolved
sulfides; and hence, by increasing odors. On the other hand,
loadings below 1,000 Ibs per acre per day will be accompanied
by dissolved sulfides concentrations less than 0.025 mg per
liter and less odor. Obviously, such a relationship would
be affected by the amount of influent sulfate, the types and
quantities of sulfide, complexing substances in the waste, and
the temperature. Hence, it would be subject to considerable
geographical variation depending on climate, factory location,
water quality, soil type, beet conditions, and so on.
Sulfide is not the only reduced substance in beet sugar waste
responsible for malodors. Volatile acids and alcohols are
malodorous, and their odor cannot be measured by merely measur-
ing sulfides. Therefore, the organoleptic or "smell" test
was systematically applied to daily samples of the waste or
effluents from various parts of the system.
All organoleptic odor products measured during the campaign
are tabulated in Appendix E-5 and the monthly mean values for
influent, anaerobic, and algae pond are plotted as a function
of month in Figure 25. As is evident from the figure, the
odor product of the influent increased during August, Septem-
ber, and October; decreased slightly in November, and then
decreased rapidly in December. In the anaerobic pond odors
55
-------
tjl
AUG
DEC
^
s
OCT
/
/
/
/
SEP
\ X
ANAEROBIC POND
MOV
ANAEROBIC POND WITH
LOADING INTERRUPTED
ALGAE POND(ALL MONTHS)
O 1-0 2-O
DISSOLVED SULFIDES,mg/f
FIGURE 24. DISSOLVED SULFIDES AS A
FUNCTION OF ABSORBED
BOD LOAD
A
\
PURPLE BACTERIA
OBSERVED
\
\
V
O INFLUENT
A ANAEROBIC
O ALGAE
I I
OCT
MONTH
FIGURE 25.
MEAN ODOR PRODUCT AS A
FUNCTION OF MONTH FOR
INFLUENT, ANAEROBIC AND
ALGAE PONDS
-------
were high in August, and decreased during September and Octo-
ber. The decrease coincided with the presence of large num-
bers of purple bacteria. The product again declined in Decem-
ber, probably because of decreased temperature.
Mean values for odor in the algae pond were initially greater
than 6 in August, declined to less than 3 in September, in-
creased during October and November, then declined to less
than 3 in November. The algae pond rarely had what would be
termed an objectionable odor, even when predators were making
inroads on the algae population. Purple sulfur bacteria were
found in the algae pond at the times when they were present
in the anaerobic pond. They too could have contributed to
the reduction in odor.
The relationship between odor product and dissolved sulfides
may be visualized by comparing these two parameters as shown
in Figure 26.
u 10
FIGURE 26.
DISSOLVED SULFIDES , mg//
MONTHLY MEAN ODOR PRODUCT AS A FUNCTION OF
MONTHLY MEAN DISSOLVED SULFIDES
57
-------
As is evident from the figure, a positive correlation exists
which probably is nonlinear. However, because of the scat-
tered data, it is not possible to conclude any point of inflec-
tion. In the case of data from influent daily samples, odor
products as high as 16 were accompanied by a "0" dissolved
sulfide determination. Inasmuch as the influent had a higher
temperature than the ponds, it seems likely that at times it
was assigned a higher odor intensity factor than the ponds.
Also, metal complexes of sulfide form more readily at high
temperatures and this would decrease the sulfide in the influ-
ent. In the case of the anaerobic pond, in one sample an
odor product of 24 was accompanied by a sulfide concentration
of 0.1 mg per liter. Thus, as is well known, and is also evi-
dent from these data, many odorous substances other than H2S
are formed in the decomposition of beet wastes. The question
then arises: What odor product would be acceptable if the
hydrogen sulfide level were almost 0? Unfortunately, the data
do not permit more than the tentative supposition that a level
of 8 or 9 may be barely acceptable.
In Figure 27 the organoleptic data for the anaerobic and algae
pond are plotted as a function of applied BOD load. Data from
the 1967 fall campaign (cf. Table 3) also are plotted. If
the exceptions of October 1967 and November 1968 are excluded
from consideration, there appears to be a linear relationship
between loading and odor product; whereas the relationship
between loading and dissolved sulfide was clearly non-linear.
The exceptions of October, 1967 and November 1968 are believed
to be due to the escape of Steffens waste into the ponds.
However, there are no data to document this supposition. If
one assumes this linear relationship to be real and that an
odor product of 8 or 9 were barely acceptable, according to
the graph an odor product of 8.5 corresponds to an ultimate
BOD loading of 1,000 Ibs per acre per day.
Nutrients: The plant nutrients measured included carbon in
the form of BOD and COD, nitrogen in the form of ammonia,
nitrate, and total nitrogen; and soluble phosphate.
During August and September, phosphate was added as phosphoric
acid to the anaerobic pond. During November and December, it
was added to the algae pond.
Daily COD and BOD values are tabulated in Appendices C-l, C-2,
and C-3. Although these results were described earlier in
conjunction with pond loading and performance characteristics,
they are presented in this section from the standpoint of
BOD and COD as nutrient parameters.
58
-------
A ANflEHOBIO POND
Q ALGAE POND
X
A
NOV68
MEAN ODOR PRODUCT
FIGURE 27.
MONTHLY MEAN ORGANOLEPTIC ODOR PRODUCT AS A
FUNCTION OF APPLIED AREAL LOADING
The monthly mean values for unfiltered COD in the influent,
the anaerobic pond and algae pond are graphed in Figure 28.
As is evident from the figure, unfiltered COD in the influent
and in the two ponds increased steadily during the fall cam-
paign. However, with respect to time, an increased fraction
of the unfiltered COD was removed in the ponds.
Mean values for filtered COD are presented as a function of
pond and month in Figure 29. From this figure, it is evident
that although the COD of filtered influent samples increased
steadily during the campaign, the COD of filtered anaerobic
pond and algae pond contents remained virtually constant be-
tween 100 and 200 mg per liter. A plot of the ratio of soluble
COD to insoluble COD is shown in Figure 30. Judging from
these results, the waste applied had a higher and higher frac-
tion of soluble decomposable matter, probably reflecting the
deterioration of beets during the fall. On the other hand,
the treated material had a decreasing amount of soluble decom-
posable matter, reflecting the effectiveness of the treatment.
In the case of the anaerobic pond, beginning with the ratio
of 45% soluble in July, an increase to 55% took place in August,
followed by a decrease to about 20% in September, October,
November, and December. In the case of the algae pond, the
COD was initially 95% in the filterable form; whereas by the
third month, only about 20% filterable or soluble COD remained.
59
-------
H
O
09
CHEMICAL OXYGEN DEMAND,
CO
W
n >
\\
\\
D >
\ \
CHEMICAL OXYGEN DEMAND, mg//
i
IT
U
- I
\\
D>
I (
I
I
I
i
i
-------
SEP OCT
MONTH
FIGURE 30.
RATIO OF MONTHLY MEAN FILTERED TO UNFILTERED
COD AS A FUNCTION OF POND AND MONTH
Soluble COD is normally about 42% carbon. Based on this
percentage, the soluble organic carbon in the influent was
253 mg per liter in July, 404 mg per liter in August, 474 mg
per liter in September, 495 mg per liter in October, 647 mg
per liter in November, and 827 mg per liter in December.
Using the same ratio, the concentrations in the anaerobic
pond averaged 50 mg per liter in July, 91 mg per liter in
August, 60 mg per liter in September, 57 mg per liter in
October, 88 mg per liter in November, and 69 mg per liter
in December. The algae pond concentration averaged 60 mg
per liter in July, 47 mg per liter in August, 49 mg per
liter in September, 44 mg per liter in October, 63 mg per
liter in November, and 55 mg per liter in December. Even
the relatively small amount of 40 mg per liter of Soluble
carbon is high when compared with tentative discharge stan-
dards for carbon in most states.
Nitrogen: Daily values for nitrate nitrogen, ammonia nitro-
gen and total nitrogen are given in Appendices F-l, F-2, and
F-3 respectively and are summarized in Table 8.
For clarity of discussion, values from Table 8 are plotted
according to nitrogen species as a function of pond and month,
Total nitrogen is plotted in Figure 31. The evidence from
Figure 31 indicates that a substantial decrease in nitrogen
occurred during decomposition of influent in the anaerobic
pond; but that as time went by, a substantial accumulation
61
-------
TABLE 8
Summary of Monthly Mean Nitrogen Values as a Function of
Species, Pond and Month - All Values Mg Per Liter as N
Month
Jul2
Aug
Sep
Oct
Nov
Dec
Sample
In
An
Al
In
An
Al
In
An
Al
In
An
Al
In
An
Al
In
An
Al
N03"
2.3
0.2
0.2
2.97
0.36
0.42
1.45
0.42
0.40
3.20
0.51
0.50
4.31
0.48
0.55
3.14
0.45
0.67
NH4*
2.0
0.2
0.1
1.64
1.18
0.68
1.17
0.58
0.30
1.38
0.79
0.54
2.76
1.63
1.31
1.54
1.30
1.10
N03" * NH4*
4.30
0.40
0.30
4.61
1.54
1.10
2.62
1.00
0.70
4.58
1.30
1.04
7.07
2.11
1.86
4.68
1.75
1.77
Total N
5.25
1.40
0.60
5.60
2.60
1.81
4.85
3.78
4.23
4.77
4.22
4.30
9.28
6.21
5.44
7.53
5.77
6.25
Diff
0.95
1.00
0.30
0.99
1.06
0.71
2.23
2.78
3.53
0.19
2.92
3.26
2.21
4.10
3.58
2.85
4.02
4.48
The difference is assumed to be organic N plus nitrite N,
the latter usually being negligible in magnitude.
'July values are singles or duplicates only, all others
are means of 10 - 20 values.
62
-------
of total nitrogen took place in the pond liquids. The con-
centration increased from about 1 mg per liter in July to
about 6 mg per liter in December.
«
6
-A-,
-a
INFLUENT
ANAEROBIC
ALGAE
/ /
/ /
* /
/
/
JUL
AU6
SEP OCT
MONTH
NOV
DEC
FIGURE 31. MONTHLY MEAN TOTAL NITROGEN VALUES AS A FUNCTION
OF POND AND MONTH
63
-------
The forms of the nitrogen are of interest. Monthly mean
values for nitrate-nitrogen as a function of pond and month
are shown in Figure 32. Influent nitrate concentrations
probably are those contained in the factory fresh water sup-
ply and are relatively small, varying from 1.5 to 4.2 mg per
liter. The data indicate, as would be expected, that essen-
tially all of this nitrate was reduced to a residual of about
one-half mg per liter which appears to be the minimum attained
in the reactions, particularly under the low temperature con-
ditions prevailing in October, November, and December.
5
O INFLUENT
A ANAEROBIC
D ALGAE
(I) SINGLE VALUES
(I)
JUL
AUG
SEP OCT
MONTH
NOV
DEC
FIGURE 32. MONTHLY MEAN VALUES FOR NITRATE NITROGEN AS A
FUNCTION OF POND AND MONTH
64
-------
Monthly mean ammonia-nitrogen values are plotted in Figure
33. Influent concentrations were erratic, and the mean
values varied from about 1.2 to about 2.8 mg per liter. A
significant decrease took place in ammonia from influent to
anaerobic pond and from anaerobic pond to algae pond. Ammonia-
nitrogen apparently increased slightly in the ponds with
respect to time. Inasmuch as the pH of the anaerobic pond
varied from 7.1 to 8.8 (cf. Appendix D-l) it is possible that
at pH values above 8.5 the sustained surface aeration to
which the anaerobic pond was subjected led to the loss of
some NH3 to the atmosphere. In each case loss of NH^ would
be a function of aeration period temperature and ammonia
concentration as well as pH.
0 INFLUENT
A--*-» ANAEROBIC
Q ALGAE
SEP OCT
MONTH
DEC
FIGURE
33. MONTHLY MEAN VALUES FOR AMMONIA NITROGEN AS A
FUNCTION OF POND AND MONTH
65
-------
Organic nitrogen was taken as the difference between total
nitrogen and the sum of nitrate and ammonia-nitrogen. The
concentration involved in this difference could also con-
ceivably involve some nitrite. These differences are plot-
ted in Figure 34. While the data are erratic, it appears
evident that the low concentrations of about 2 mg per liter
in the influent were greatly increased in the ponds. The
increase probably was a result of the accumulation of cellu-
lar material which ultimately led to an increase in organic
N plus nitrite from about 1 mg per liter to more than 4 mg
per liter.
~ i
O INFLUENT
A ANAEROBIC
D ALGAE
SEP OCT
MONTH
FIGURE 34. MONTHLY MEAN VALUES FOR ORGANIC + NITRITE
NITROGEN AS A FUNCTION OF POND AND MONTH
66
-------
From an overall standpoint, the quantity of nitrogen in the
waste was very low when compared with the amount of carbon
in the waste. A tabulation of filtered COD, organic carbon,
total nitrogen, carbon nitrogen ratios and monthly mean
phosphorus concentration is presented in Table 9. Table 9
provides some degree of visualization of nutrient relation-
ships in the system.
If one accepts the concept that organic matter is approaching
stability when the carbon nitrogen ratio reaches 10 or less,
according to Table 9, stability was never approached in the
anaerobic pond and was approached only twice in the algae
pond in October and again in December.
It should be noted that with the exception of influent, the
phosphorus concentration shown in Table 9 resulted from the
addition of phosphorus to the system. As stated earlier,
during August and September, phosphate was added to the
anaerobic pond as phosphoric acid and during late October,
November, and December, it was added to the algae pond.
Influent phosphorus without phosphate addition varied from
0 to 4.5 mg per liter with monthly mean values varying from
0.57 in December to 1.53 in November. This quantity of
influent phosphorus is probably too low to support high rates
of microbial decomposition, especially for high BOD wastes.
It should be noted that during the addition of phosphate to
the anaerobic pond, phosphate was transferred to the algae
pond. However, the phosphate underwent a depletion of some
type in the algae pond, so that without direct addition a
level of about 0.5 mg per liter prevailed in the algae pond.
According to the findings of Zabat (6), and others, this
would provide only sufficient P for the growth of about 50
mg per liter of algae. On the other hand, when phosphate
was added to the algae pond directly, little phosphate
appeared in the anaerobic pond, indicating that it did not
remain in solution long enough to be transferred back to the
anaerobic pond with the recirculant in any significant quan-
tities. These facts emphasize the concept that in nutrient
addition, the point of addition as well as quantity added
are highly significant.
Organisms: During the course of the experiments, microscopic
observations of the microorganisms in the ponds were made as
frequently as possible. The quantities of algae and other
organisms were estimated by means of visual microscopic enu-
meration and by means of packed volume determinations.
The results of the enumerations are tabulated on a daily
basis in Appendix G. Appendix G-l consists of daily algae
counts and monthly means of the daily counts. A summary
67
-------
TABLE 9
Nutrient Relationships
Month
Aug
Sep
Oct
Nov
Dec
Sample
In
An
Al
In
An
Al
In
An
Al
In
An
Al
In
An
Al
Filt
COD
mg/1
961
217
112
1128
144
116
1180
137
104
1541
209
150
1969
165
130
C1
mg/1
404
91
47
474
60
49
495
57
44
647
88
63
827
69
55
N2
mg/1
5.6
2.6
1.8
4.8
3.8
4.2
4.8
4.2
4.3
9.3
6.2
5.4
7.5
5.8
6.2
C/N
72
35
26
99
16
12
103
14
10
70
14
12
110
12
9
P3
mg/1
1.5
13.9
7.3
0.78
2.04
1.57
0.79
1.25
0.54
1.53
1.43
9.30
0.57
0.43
7.10
X0.42 x Filt COD
o
Total Nitrogen in unfiltered samples. No extra
nitrogen was added during the course of these experiments.
P was added at the approximate average rate of 5 mg/liter.
Because of poor flow control* phosphorus levels were sporadic
but in excess of normal requirements.
68
-------
of these means as a function of pond and month is presented
in Figure 35. As is evident from the figure, the mean algae
count in the anaerobic pond was about 400,000 per ml and
remained fairly constant. The count in the algae pond fluc-
tuated greatly, being relatively low in August, increasing
in September, again decreasing in October, and then increas-
ing in November and December. The mean value was approximately
1 x 106 cells per ml.
o
1.0
ID
O
O
LU
O
-1
0.5
-A ANAEROBIC POND
O ALGAE POND
D
A
\
a
A
AUG
SEP
OCT
MONTH
NOV
DEC
FIGURE 35.
MONTHLY MEAN ALGAE COUNTS AS A FUNCTION OF
POND AND MONTH
69
-------
Results of daily determinations of the packed volume of
algae cells in terms of ml per liter wet weight are tabula-
ted in Appendix G-2. As noted previously, these volumes
were estimated as percentages of the total packed volume of
solids. Monthly mean values for the algae volumes are plot-
ted in Figure 36 as a function of pond and month. The pat-
tern for packed volume was roughly the same as that for the
algae count, except that no drop in packed solids volume
occurred in October in the algae pond. Such a drop in packed
solids volume did occur in the anaerobic pond.
3.0
9 2.0
-J
O
CO
A ANAEROBIC POND
-D ALGAE POND
TO ESTIMATE DRY WEIGHT
IN mg/lifer , MULTIPLY
PACKED VOLUME (ml/liter) K 140
D
/*
\
\
\
AUG
SEP
OCT
MONTH
NOV
DEC
FIGURE 36.
MONTHLY MEAN PACKED VOLUME OF CENTRIFUGED ALGAL
SOLIDS AS A FUNCTION OF MONTH AND POND
70
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There is a fairly fixed ratio between packed volume of green
algae cells in ml per liter and dry weight in mg per liter.
As indicated in the note in Figure 36, to estimate dry weight
in mg per liter, one should multiply the packed volume of
algae in ml per liter by 140. Thus, a packed volume of 2 ml
per liter of algae is equivalent to a dry weight of 280 mg
per liter of algae. Inasmuch as the organic-N equivalent
to this data was only about 3.5 mg per liter, and green algae
normally contain a minimum of 6% nitrogen dry weight, the
algae were either extremely nitrogen deficient, or the mater-
ial measured was not entirely green algae. A fixed ratio
also exists between the dry weight of algae cells and the
amount of oxygen produced as a result of algae growth. The
ratio is 1.6 mg of 02 per mg of algae. Thus, a packed volume
of 2 ml of algae per liter indicates that 2 x 1.6 x 140 = 450
mg of 02 per liter of culture were produced during growth of
the algae. If 20 days were required to accomplish such growth,
the rate would be 22.5 mg per liter per day, which for a
three-foot depth could be equivalent to 200 Ibs per acre per
day. While algae appeared in the anaerobic pond, they were
brought there by recirculant and their growth in the anaero-
bic pond was probably small due to poor light conditions.
There is little question that the changing numbers and weights
of algae present in the ponds in August and October were func-
tions of the proliferation of predators at the expense of
algae in the ponds. Two main types of predators invaded the
ponds at different times. They reached their peak numbers
about two months apartdaphnia and related organisms in August
and rotifers in October.
Tabulations of such daily observations as are available for
daphnia are presented in Appendix G-3 and the monthly mean
values are plotted as a function of pond and month in Figure
37. As indicated by the figure, daphnia were found in the
algae pond during all months, but were at their peak concen-
tration in August. Mean concentrations as high as 20 of
these relatively large organisms per ml were observed. Be-
cause of recirculation, the organisms when abundant, could
be found in the anaerobic pond as well as in the aerobic
pond, although their numbers were relatively small in the
anaerobic pond. Apparently they were unable to survive in
the generally anaerobic environment of the anaerobic pond.
Observations of rotifer numbers are tabulated in Appendix
G-4 and the monthly mean values are plotted in Figure 38.
As is evident from the figure, the number of organisms rose
to a peak during October in the algae pond and in the anaero-
bic pond. Those in the anaerobic pond probably were drawn
there with the recirculation stream, but were able to survive
71
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ZL
H
o
cj
LO
-J
THOUSANDS OF ORGANISMS PER LITER
x
X
X
D >
Cl >
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m 35
8
H
a
a
THOUSANDS OF ORGANISMS PER ML
00
O > S
bd w O
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C** h^
O 2
1-3 pd
H >
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-------
in considerable numbers in spite of the low oxygen levels
in the anaerobic pond. The decline in numbers, both of
rotifers and daphnia during November and December, probably
was a result of their sensitivity to lowered temperatures
in the ponds. The decline was accompanied by increased
numbers of algae. Although it is not apparent from the mean
values, daily values indicate that there were several pulses
of growth and die-away of the organisms during each month.
The pulses of predator growth were accompanied by decreases
in algae numbers and volumes, and in the concentration of
dissolved oxygen in the algae pond. These details in the
daily data are obliterated by taking the mean values over
a monthly period.
During September and October, purple sulfur bacteria were
visibly prominent in the anaerobic pond, and due to recir-
culation, were also swept into the algae pond. The data
collected on these organisms are tabulated in Appendix G-5
and mean values are plotted as a function of pond and month
in Figure 39. As evidenced by the figure and appendix, the
thiocystis-like Thiopedia and Chromatium species attained
enormous numbers of organisms (as high as 50 million per ml)
and their packed volumes in some cases were almost as great
in the anaerobic pond as those for the algae in the algae pond
Algae types and their occurrence by pond and month are tabu-
lated in Appendix H and a summary of species and occurrence
is presented in Table 10. According to the table, 30 species
of algae were endemic in the ponds at various times; 19 spe-
cies occurred in the anaerobic pond; and 29 species occurred
in the algae pond. The most frequently observed species in
the algae pond in descending order were members of the genera
Chlorella, Nitzchia, Oscillatoria, Scenedesmus, Euglena,
Phacus, and Chlorococcum.With the exception of species of
Chlorococcum, species of these genera also were predominant
in the anaerobic pond. The greatest diversity of species
occurred in September in both ponds, with October and August
following in descending order.
Gas Production: Daily gas production from the anaerobic pond
is tabulated in Appendix G-6 and mean monthly production is
plotted in Figure 40 as a function of the mean monthly tem-
perature in the anaerobic pond. As noted previously, because
of a lack of time and gas, an intended program of gas analy-
sis could not be initiated and the gas composition was not
precisely determined. It was superficially determined by a
simple ignition test, to contain a substantial combustible
fraction.
73
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I r ~
BACTERIAL SPECIES:
THIOCVSTIS-LIKE THIOPEDIA
CHROMATIUM SR
A ANAEROBIC POND
D ALGAE POND
\
\
\
\
I YL
ANAEROBIC POND
BRONSON COLLECTOR
SEP
,POINT OF INFLECTION
T=I3.5°C
DCT
MONTH
MONTHLY MEAN POND TEMPERATURE,"C
FIGURE 39.
MONTHLY MEAN PURPLE
SULFUR BACTERIA COUNT
AS A FUNCTION OF POND
AND MONTH
FIGURE 40.
RELATIONSHIP BETWEEN GAS
PRODUCTION AND TEMPERATURE
FOR VARIOUS MONTHS
-------
TABI£ 10
Algal Species in Che Ponds and the Percentage of Samples Examined
in which they Occurred as a Flmction of Pond and Month
Algal Species
Occurrence %
of Sample
Oscillatoria
Scene desmus
Ch lorococcum
NiCzchia
Ch lor el la
Euglena
Phacus
Fragilaria
Anabaena
Pyrobotrys
Stigeoclonium
Actinastrum
Coelastrum
Cyclotella
Tetraedron
Closterium
Ankistrodesmus
Selenastrum
Anabaenopsis
Diatoma
Ch lor ococcone i s
Oocystis
Microspora
Gomphosphaeria
Microcystis
StephanodlscuS
Pa Intel la
Com pH one ma
Staurastrum
Carter! a
Anaerobic
Month
Aug
92
74
7
92
100
78
52
7
30
26
Sep
87
77
96
96
73
27
9
36
55
5
5
18
14
5
5
18
36
Oct
86
64
93
93
64
29
71
7
7
29
Nov
50
50
80
100
40
20
10
10
Dec
100
33
33
67
33
33
33
33
Algae
Month
Aug
92
85
11
96
100
96
67
4
26
26
7
Sep
77
91
55
91
91
82
50
36
18
5
55
18
14
14
18
23
5
5
14
27
9
5
9
14
18
14
5
5
Oct
87
80
13
87
100
80
33
7
66
7
7
13
53
7
Nov
60
80
40
90
100
80
30
30
10
30
10
Dec
60
80
80
80
80
60
40
20
20
20
75
-------
As is indicated by the figure, gas production was apparently
quite low during August and September. On the other hand,
the figure indicates that beginning in October, gas produc-
tion apparently was severely limited by temperature if not
by other factors. A comparison of gas production (Appendix
G-6) on a day-to-day basis with temperature in the anaerobic
pond (Appendix A-3) indicates that a definite inflection point
occurred when the pond temperature reached 13.5°C. Pond tem-
peratures were actually measured near the pond surface,
whereas gas emission was primarily from the pond bottom and
therefore sensitive to bottom temperature. Although bottom
temperature was not measured on November 20, it probably was
at least 1.5°C less than that of the water near the surface.
Thus, the temperature-gas production relationship described
by Bronson et al. (7) in which gas production increases
linearly witE temperature above 15°C is closely approximated
by these data.
Nutrient Studies: In the special fertilizer study, 12-liter
vessels were operated during November, 1968, by starting
with algae pond liquid incubated in laboratory light and
pouring off one liter each day and replacing the liquid with
"spiked" algae pond effluent. Incubation was at room tem-
perature and illumination was with 30-watt fluorescent lamps.
The additions of fertilizing materials consisted of potassium
phosphate, ammonium phosphate, ammonium nitrate, sodium ni-
trate, phosphoric acid, and 15-8-4 commercial fertilizer. An
algae pond effluent liquid control was also incubated and
monitored for growth. The enrichments were added to provide
approximately 5 mg per liter of the fertilizing chemical in
the final solution. The systems were initially buffered
with 50 ml of sodium carbonate solution which apparently was
effective because the pH of all cultures remained between
7.5 and 8.5 during the entire test. Although the test was
extended for about 25 days, problems with rotifers and purple
sulfur bacteria became overwhelming during the last 10 days
of the test. Therefore, the results after 15 days of incu-
bation at room temperature in the light are taken as most
representative. These data in terms of packed volume are
shown in Table 11. As shown in the table, on the 15th day
best growth was found to have taken place in ammonium phos-
phate, followed by potassium phosphate, ammonium nitrate,
commercial fertilizer control, sodium nitrate, and phosphoric
acid in the order named. A reference to Table 9 shows that
the algae pond effluent averaged 9.2 mg per liter P during
November; hence, it is not surprising that phosphorus did
little to enhance growth in the control. In view of this,
it is somewhat surprising that the addition of potassium
phosphate gave such a high assay growth response. The overall
76
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results indicate that ammonia and perhaps phosphate are
essential fertilizers and that potassium should be reexa-
mined, particularly in view of the fact that as : shown in
Table 11, at least one sampled beet waste initially con-
tained as much as 88 mg per liter of potassium.
TABLE 11
Nutrient Spiking Experiment
NO.
1
2
3
4
5
6
7
Fertilizer Applied at
About 5 Mg Per Liter
Control* Pond 4
Potassium Phosphate
Ammonium Phosphate
Ammonium Nitrate
Sodium Nitrate
Phosphoric Acid
(15-8-4) Commercial
Fertilizer
PH
7.7
7.9
8.1
8.1
7.9
8.0
8.0
15-Day Packed
Volume Mg Per Liter
0.6
2.2
4.8
2.0
0.5
0.5
0.7
*Algae Pond Effluent
77
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-------
SECTION VI
DISCUSSION
The results of this study show very clearly the extensive
variations in waste strength, pH, and nutritional charac-
teristics of beet sugar factory wastes. The seasonal
variations in waste strength are so large that it would
be impossible to design an effective unbuffered, short
detention waste treatment system "or steady-state or
average conditions. The degree of variability is apparent
when one examines the unfiltered COD data for influent in
Appendix C-l, in which values vary from 550 mg per liter
in August to 3643 mg per liter in KvVember, and 3380 mg
per liter in December; and when one considers the influent
pH values shown in Appendix D-l in which the variation is
from 5.7 to 11.6.
No short-detention period biological system lacking in
buffer capacity could withstand sudden shifts in nutrient
and pH of the magnitude found without violent upsets or
complete failure in essential microbial growth. A cir-
culated algae pond could tolerate the changes in pH, but
could not tolerate the changes in loading. Activated
sludge units could not tolerate either the change in pH or
the change in loading. Trickling filter units could per-
haps tolerate the variable loading but could not tolerate
the variable pH. Thus, activated sludge units, circulated
algae ponds, and trickling filters, if considered in the
design of primary units of systems for factory waste would
have to be designed for that loading which could not be
exceeded at least 95% of the time. They would have to be
continuously monitored and protected from changes in pH.
Design criteria such as these would make such treatment
extremely expensive.
The obvious corollary to these statements is that a mas-
sive primary buffer system is vital to any successful and
economical biological treatment of beet sugar factory waste.
In considering the design characteristics of a buffering
system, the anaerobic pond is an obvious choice because
its simple earthwork construction, large size and relatively
long detention period will, according to our evidence,
buffer almost any extreme variation in pH which might
occur in a factory effluent and would dampen changes in
BOD. At the same time it would be relatively inexpensive.
In view of the necessity of a buffer pond, it is fortunate
that in addition to acting as a buffer, a substantial
degree of waste treatment is attained in an anaerobic pond.
79
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It was found during the course of these investigations that
in the anaerobic pond BOD removal was directly proportional
to BOD loading in the range of 500 to 2,000 Ibs of BOD per
acre per day. At loadings above 2,000 Ibs, removal effi-
ciency is believed to decline. The removals as found are
related to loading approximately as follows;
R = 0.8 L
(2)
in which L is the ultimate BOD load between 500 and 2,000
Ibs per acre per day and R is the ultimate BOD removed.
Of course, both R and L should be expressed in the same
units. Thus, it appears that an anaerobic pond loaded at
1,000 Ibs of ultimate BOD per acre per day will produce
an effluent containing 200 Ibs of ultimate BOD per acre
per day and one loaded at 2,000 Ibs of ultimate BOD per
acre per day will produce an effluent having 400 Ibs of
ultimate BOD per acre per day. If BOD loading were the
only criterion of performance, the obvious choice of recom-
mended design loading would be 2,000 Ibs of ultimate BOD
per acre per day. It is an unfortunate fact that when the
study pond received BOD loadings as high as 2,000 Ibs per
acre per day, it was continuously malodorous; hence, some
criterion other than Equation 2 is required on which to
base a decision regarding an upper limit for anaerobic
pond loading. Two main criteria seem to be available:
odor level and acceptable discharge BOD.
Inasmuch as odor is one of the most urgent problems, odor
level will be discussed first. In the case of the anaero-
bic pond, the data accumulated during this study were not
sufficiently refined for a final conclusion; but from in-
spection of Figures 24, 25, 26 and 27, one is left with
the general impression that for normal beet waste, an odor
product of lower than 8 to 10 may be barely acceptable.
An odor product much above 10 is definitely unacceptable
because it is always accompanied by sulfide concentrations
above 0.025 which are always detectable. An allowable
odor product of 10 would permit sulfide odors of 2 inten-
sity or foul odors of intensity 1.7 some of the time. How-
ever, such low intensities would imply very little carrying
power for the odors; or in air, odors of such intensity
would be quickly diluted to subliminal levels as a func-
tion of distance from the ponding site. It seems quite
certain that odor products of 8 or less would be acceptable
for anaerobic ponds because these levels were frequently
reported for the algae pond, which rarely had a high odor
product in laboratory samples and was never described as
objectionable in pond-side observations.
In the plot of odor product vs loading, there appears to
be a straight-line relationship with two observed exceptions'
80
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the October 1967 data and the November 1968 data. These
data come from periods when there were serious interrup-
tions in flow, and consequently, rapid changes in the en-
vironment. Total nitrogen concentrations were also high
during these periods, possibly due to the discharge of
Steffens waste. Steffens waste is, of course, notorious
for its ability to produce vile odors when impounded, and
"Steffens waste spills" are always accompanied by sudden
increases in odor in ponding systems. There was, however,
no reported incidence of a "spill" and no report that Stef-
fens waste had been bled into the effluent. Thus, it can
only be concluded at this time that a load of 1,000 Ibs of
ultimate BOD per acre per day may be acceptable in an anaero-
bic pond when mechanical surface aeration is applied to
the extent of meeting one-third of the applied BOD, and when
the effluent is discharged into a functional aerobic or
algae pond from which there is a recycle of about 1 Q and
in which algae are growing and producing oxygen.
With regard to acceptable discharge BOD, effluents from the
anaerobic pond varied from 120 mg per liter at a load of
500 Ibs per acre per day to in excess of 400 mg per liter
at a load of 2,000 Ibs per acre per day. Water of this
quality would be useless and its discharge illegal without
extensive additional treatment.
The additional treatment studied involved both facultative
and algae ponding. At BOD levels ranging from 50 to 200
Ibs per acre per day as noted previously, odor products in
the systems studied tended to be 6 or less and objectionable
odors at the pond side were minimal.
With regard to the application of BOD criteria to the facul-
tative pond and algae pond, an examination of the available
data is best aided by plotting mean final effluent BOD as a
function of mean BOD loading. Such a plot is shown in
Figure 41. As is evident from the figure, the BOD of un-
filtered effluents was not affected by loadings up to 100
Ibs per acre per day while the BOD of filtered effluents
was not affected by loadings up to 180 Ibs per acre per
day, but the unfiltered BOD both from the facultative pond
in 1967 and the algae pond in 1968, would not be acceptable
in the average aquatic environment under the currently pro-
posed water quality standards (8).
It is important to note that decreased BOD loadings below
100 Ibs per acre per day did not appear to influence the
effluent BOD, probably because most of the BOD involved
in these samples was of a suspended nature, either in the
form of colloidal sulfides, algae cells, or of bacterial
81
-------
cells. This was true because the algae pond was continuously
mechanically mixed and samples were drawn directly from the
mixing system. The suspended nature of the BOD is demon-
strated by the fact that the BOD of the algae pond effluent
was reduced from levels of 150 to 190 mg per liter to 10 to
13 mg per liter by filtration. In view of these relation-
ships, it is apparent that the residual BOD in the algae
pond effluent was due to BOD which could have been removed.
Therefore, had the removal been effected, obviously greater
efficiencies would have been attained.
200
-------
Merely decreasing the BOD loading below 100 Ibs per acre per
day did nothing to improve effluent quality. On the other
hand, filtration improved effluent quality dramatically,
even at loadings of 180 Ibs per acre per day. An examination
of suspended solids data shows that effluent suspended solids
often exceeded a concentration of 500 mg per liter with over
75% volatile matter. Thus, apparently an improved unfiltered
effluent could not be attained by reduced loading. It should
be noted, however, that in the case of the algae pond, load-
ings between 100 and 180 Ibs per acre per day yielded efflu-
ents which when unfiltered had BOD levels between 80 and 190
mg per liter respectively. Thus, while a loading of 100 Ibs
per acre per day was associated with unsuitable effluents,
higher loadings produced effluents substantially more un-
suitable. The apparent conclusion is that aerated-anaerobic
ponding followed by either facultative or algae ponding
without further treatment did not produce an effluent suit-
able for discharge, regardless of the degree to which loading
is decreased. Aside from the alternative of intensive mechani-
cal aeration (which will treat, but not dispose of water),
one is confronted with only two clear alternatives for com-
plete disposal: 1) to use facultative secondary ponds
loaded at 100 Ibs per acre per day or less and to dispose
of the final effluent on land owned by the Factory from
which there is no discharge; or 2) to use a more intensive
form of secondary ponding and to remove suspended solids from
final effluents prior to discharge by filtration or some other
method of separation which will remove the fine suspended
solids which contribute most of the effluent BOD. The dis-
charge of filtered facultative pond effluent is another pos-
sible alternative, but no study was made of facultative pond
effluents which had been filtered.
Intensive secondary ponding could involve the use of mixed
algae ponds of the type studied, or an even more intensive
form of algae production. For example, where climate per-
mitted, the algae pond could be optimized for photosynthe-
tic oxygenation with an average production of about 200 Ibs
of oxygen and 120 Ibs of algae per acre per day. Under these
conditions, it is conceivable that the value of the filtered
solids could pay for the cost of filtration. However, this
would require much more study. Allowable loading would then
be about 200 Ibs per acre per day, and following separation,
the discharge would meet rigorous quality standards. One
may then logically say, "Why discharge such high quality
water, particularly in water-short areas?" If the quality
of a filtered discharge is high as indicated in Figure 41,
reuse in the factory by recycle is a worthwhile considera-
tion whenever filtration is used. Obviously, the less new
water brought into a factory, the less it will have to dis-
charge. On the other hand, because of the high water content
83
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of beets, it seems inevitable that factories will always be
forced to discharge or otherwise dispose of large amounts of
excess water regardless of recovery practice.
Based on the criteria of 80% BOD removal in a primary anaero-
bic pond and a loading of 200 Ibs BOD per acre per day in
an algae pond, one can explore the areal requirements for
treatment in an idealized anaerobic-algae system. To have
a basis for calculation, a 4.5-K ton factory discharging
36,000 Ibs of BOD per day is assumed. It is also assumed
that excessive odors will occur when the aerated-anaerobic
pond loading exceeds 1,000 Ibs of BOD per acre per day. If
a load of 500 Ibs of BOD were applied to the anaerobic pond,
the area of anaerobic pond would be 72 acres, the discharge
would be 100 Ibs per acre per day or 7,200 Ibs, and 36 acres
of algae pond would be required for an aggregate area of 108
acres. If a load of 1,000 Ibs per acre is applied to the
anaerobic pond, the total loading of 36,000 Ibs will require
36 acres. The anaerobic pond effluent will contain 7,200
Ibs of BOD and therefore will require 37 acres of algae pond.
The aggregate area in this second case would be 72 acres.
If a' load of 2,000 Ibs of BOD per acre were used, 18 acres
of anaerobic pond would be required for anaerobic treatment,
but odors would be severe and a stronger waste would be dis-
charged to the algae pond. Although according to Equation
2 the effluent BOD would be 7,200 Ibs, and would require 36
acres of algae pond, in reality, because of bacterial and sul-
fide turbidity, an area larger than 36 acressay 40 acres--
probably would be required if the effluent were to be fully
oxidized. Moreover, strong odors would occur.
A plot of these relationships is presented in Figure 42.
From the figure, it becomes evident that with the assump-
tions described, the minimum area required for odor-free
treatment of factory waste from, a 4.5-K ton factory by an
aerated anaerobic-algae system would be about 72 acres.
Higher loadings would be accompanied by severe odors and, as
indicated by the dotted portion of the top curve, would
require more algae ponds for aeration. Lower loadings would,
of course, require more area, the area increasing as the
areal loading is decreased.
As an alternative to using facultative or algae ponding as
the secondary system, one should consider the alternatives
of more intensive aeration of primary ponds or the use of
aerated secondary ponds. The possibility of applying addi-
tional surface aeration in an anaerobic pond to prevent odors
and to permit higher areal loadings and decreased pond sur-
face area is worthy of consideration, and was to some extent
examined experimentally. In the study with a 5 HP floating
surface aerator, it was found that as long as the dissolved
84
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20
ADDITIONAL AREA REQUIRED TO PRODUCE OXYGEN
TO OXIDIZE REDUCED INORGANIC SUBSTANCES AND
TO COMPENSATE FOR COLLOIDAL TURBIDITY
DESIGN OPTIMUM FOR EXPERIMENTAL SYSTEM
PRIMARY
OR
ANAEROBIC
. PONDS
(SURFACE AERATED
FOR ODOR CONTROL)
200
300
POND AREA .acres
FIGURE 42.
MAIN WASTE PONDING AREA REQUIRED FOR 4.5 K TON
FACTORY
oxygen remained zero, oxygen entered the pond at the rate
of 307 Ibs per day due to the 5 HP aerator. Odor emission,
however, appeared to be a function of the amount of unoxi-
dized material remaining, rather than a function of the rate
of aeration. Thus, if one were to go from a loading of 1,000
Ibs per acre per day to a double loading of 2,000 Ibs per
acre per day, control of odor probably could not be .attained
by aerating at twice the 307 Ibs per acre per day, i.e., 614
Ibs per acre per day. Instead, aeration would have to be
at a rate of 1,000 + 307 Ibs or 1,307 Ibs per acre per day.
Thus, it is believed that to double loadings in the system
studied, aeration would have to be increased fourfold to
prevent odors. The savings in area would thus have to be ,
evaluated in terms of the cost of one 20-HP aerator operating
continuously for each acre of secondary pond replaced. Thus,
the possibility of decreasing area,by going to loadings higher
than 1,000 Ibs per acre per day is not as attractive as it
might at first seem.
With regard to replacement of secondary facultative or algae ,
ponds with aerated secondary ponds, it will be assumed that
85
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the mechanically induced reaeration rates obtained in oxygen-
free ponds do not apply and that the dissolved oxygen level
for discharged or recovered water should be about 4 mg per
liter. Under such conditions, according to the manufacturers
brochure (5), a surface aerator provides 1.8 Ibs of 09 per
HP hour. At this rate, each 5 HP aerator will contribute
220 Ibs of 02 per day. This is approximately the amount
of oxygen contributed by one acre of high-rate pond. By
itself, a 5 HP aerator would probably be less costly than
one acre of pond, but inasmuch as wastewater storage for
reuse or disposal may be an essential part of any practical
system, a substantial pond area may be required anyway, and
all of the pond costs therefore need not be allocated against
the aeration process.
Aeration due to flow mixing also is worthy of consideration
as a source of supplemental aeration. This form of aeration
is often referred to as eddy diffusion aeration because it
is dependent on renewal of the surface resulting from eddies
generated as the water moves past small discontinuities at
the pond bottom. Surface aeration, of course, does not occur
when the water is saturated with oxygen as occurs due to
photosynthesis. However, when photosynthesis is not opera-
tive (at night, on cloudy days or under winter conditions),
eddy diffusion aeration becomes functional. A pond four feet
deep with the liquid moving around a closed circuit at a
velocity of one foot per second and containing no free dis-
solved oxygen will require about 50 HP hours per acre and
absorb about 100 Ibs of oxygen per acre per day through sur-
face aeration. Although this amount of oxygen is small com-
pared with that attainable through mechanical surface aera-
tion, it is a method which is compatable with photosynthetic
oxygenation. If the liquid contains growing algae and essen-
tial nutrients, the algae may produce over 200 Ibs of oxygen
per acre per day through photosynthesis, and the dissolved
oxygen level will always be positive and frequently near
saturation. Oxygen produced photosynthetically, of course,
does not depend upon an oxygen deficit for input; and hence,
never is accompanied by vile odors. Odors could result if
the pond were so severely overloaded on a sustained basis
that algae were unable to grow. However, if algae either
fail to grow for one reason or another or are killed by tox-
ins or predators, eddy diffusion aeration in the flow system
will provide for the absorption of sufficient oxygen by the
pond to keep it from producing vile odors of high intensity,
providing the loading does not exceed 200 Ibs per acre per
day. Thus, flow mixing is an excellent backup for photosyn-
thetic oxygenation; but it is not as efficient an aeration
system as is mechanical surface aeration.
86
-------
Provision for any form of biological treatment requires in
addition to a mild and stable environment, adequate nutri-
tional conditions. Flume water usually contains about 400
mg per liter of carbon as C, about 15 mg per liter of avail-
able nitrogen as N, and about 3 mg per liter of soluble phos-
phate as P. Rapidly growing bacteria are about 40% carbon
as C, 10% nitrogen as N, and 1.5% phosphorus as P, and radidly
growing microalgae are about 55% carbon as C, 8% nitrogen as
N, and 1% phosphorus as P. Based on these percentages, flume
water contains enough carbon to support 725 mg per liter of
algae, enough nitrogen to support 188 mg per liter of algae,
and enough phosphorus to support 300 mg per liter of algae.
It is clear that compared with carbon, there is a deficit
in both nitrogen and phosphorus, and that 725/188 x 15 or
about 88 mg per liter of N and 725/300 x 3 or about 7.25
mg per liter of P would be required to permit incorporation
of all of the organic carbon into algae. Thus, 73 mg per
liter of N and 4.25 mg per liter of P would have to be added.
A less expensive alternative would be to remove carbon by
processes other than by photosynthesis, and thereby decrease
the carbon to a point at which it is in balance with the
nitrogen and phosphorus for algae growth. By so doing, it
would not be necessary to provide supplementary nitrogen and
phosphorus.
Several processes observed in the anaerobic pond during this
study are accompanied by loss of considerable carbon dioxide
to the atmosphere. This is probably especially true in the
case of mechanically aerated ponds. For example, the satis-
faction of 307 Ibs of BOD per acre each day by aeration theo-
retically led to the evolution of 450 Ibs of C02 per acre.
Thus, probably 122 Ibs of carbon per acre per day was lost
to the air. This alone would constitute a loss of 222 Ibs
of carbonaceous AGP. Following this line of reasoning, if
two-thirds of the BOD had been met by aeration, sufficient
carbon would have been lost to permit the balance to be in-
corporated in algae with no need to add nitrogen or phos-
phorus .
Methane fermentation also is a potential method for decreas-
ing the carbon content of the waste. As noted earlier, gas
production in the system was extremely low, and did not
establish itself appreciably in spite of the presence of
large amounts of carbon, highly anaerobic conditions, ade-
quate temperatures, and sustained periods of inundation.
Under the warmest temperatures encountered in the study, 250
ft3 of gas per acre per day were emitted from the bottom
of the anaerobic pond. Although analyses were not made,
judging from past experience (7) this gas probably contained
about 50% methane, of which 75% is carbon. Thus, for the
87
-------
one acre pond, only about 4 Ibs of carbon were lost daily
by fermentation. If methane production rates equal to those
in domestic sewage ponds had been attained, as much as 200
Ibs per acre of carbon would have been lost daily in the
form of methane. However, this did not occur in the system.
As to why it did not occur, it is possible that methane
bacteria found it difficult to survive in a pond in which
surface aeration was in progress. However, even before
the aerator was installed, as noted in Progress Report III
(1), there was a dearth of fermentation. Thus, further
studies would be required to substantiate aeration inter-
ference. Another hypothesis advanced for poor fermentation
is the excess of HnS or sulfides in the system due to vigor-
ous sulfate reduction in the anaerobic pond as discussed
under Chemical Changes. Sulfide is known to be toxic to
methane bacteria even in moderate concentrations. Thus, car-
bon elimination by methane fermentation could have been inhi-
bited by this mechanism.
In order to continue with the discussion of carbon, nitrogen,
and phosphorus ratio and the need for nutrient supplementa-
tion, it is necessary to digress slightly to explore sulfate
reduction in some detail, since this is also a potentially
significant way in which carbon may be lost.
The overall reaction involved in production of H2S from sul-
fate using organic matter as an energy source is approximately
H2S04 + 2CH20 organic! H2S +
2C0
(3)
According to the data on sulfate reduction shown in Figure
21, as much as 208 mg per liter (average about 140 mg per
liter) of sulfate was reduced in the anaerobic pond during
the five-month period of observation. Based on the stoichio-
chemistry of equation (3), the reduction of 140 mg per liter
of sulfate would have involved the oxidation of 88 mg per
liter of organic matter and the production of 50 mg per liter
of H2S and 128 mg per liter of C09 or 35 mg per liter of
carbon. A substantial fraction of this CC>2 was doubtlessly
incorporated in the alkalinity of the water in the anaerobic
pond.
One may question why that although 50 mg per liter of H2S were
produced, a maximum of only 5-6 mg per liter of HS~ were re-
covered. This imbalance may be explained by the supposition
that as soon as HS~ was produced, it could have reacted in
several ways. It could have reacted with magnesium or other
metals in the system to produce insoluble metal sulfides
which of course were not measured in the dissolved sulfide
88
-------
determination; it could have been utilized by sulfur bacteria.
Emission into the air was evidenced by the presence of sul-
fide odors about the anaerobic pond. However, the magnitude
of emission must have been small because at the pH of 7.5
to 8 (a level almost always found in the anaerobic pond),
most of the sulfide would be present as the HS~ species rather
than as H2S.
Inasmuch as there is no H^S normally in the air, the reaction
involved in the emission of H^S occurs spontaneously whenever
dissolved H2S exists in solution. The quantity remaining in
solution is mainly a function of pH. The reaction is:
HS'
Acid
Basic
(4)
At pH 4 practically all of the material is in the H2S or
gaseous form and emission rates are high. At pH 6, half is
in the gaseous form and half in the ionic HS~ form; and at
pH 7.5, about 90% is in the ionic form and 10% in gaseous form
and emission rates are low. At pH 9.5, almost all material
is in the ionic form and there is no emission of HjS. Thus,
in view of the pH levels in the anaerobic pond (cf. Figure
10), the possibility is slight that all I^S would have been
emitted due to aeration during August, September, October,
and November when the pH was higher. Yet, a substantial frac-
tion could have been lost that way during December when the
pH was low. The curves in Figure 21 give evidence that some
sulfides were probably carried over into the algae pond as
a reduced complex which later was oxidized to sulfate. This
is evidenced by the fact that the sulfate concentraion in the
algae pond was consistently greater than it was in the anaero-
bic pond.
With regard to the loss of sulfide to sulfur bacteria, accord-
ing to the data in Appendix G-5, there were numerous sulfur
bacteria in the pond from time to time although their bio-
mass was small. However, several parts per million of sul-
fide could have been converted to elemental sulfur by these
bacteria.
Returning to the specific question of carbon losses, accord-
ing to Equation 3, the overall conversion of carbon due to
sulfate reduction must have been on the order of 128 mg per
liter as CC>2 or 35 mg per liter as carbon. Overall then, more
than one-half of the carbon introduced must have been converted
to CO2.
Another check on carbon transformation is provided by the COD
data. According to COD information (see Table 5), the overall
89
-------
reduction in unfiltered COD for the anaerobic pond averaged
1,150 mg per liter. Based on the classical oxidation equation:
CH20 + 02
C02 + H20 (5)
For which the combining weights are:
30 + 32
12 + 32 + 18
An average carbon release of 460 mg per liter in the anaero-
bic pond would have occurred due to oxidation of 1,150 mg
per liter of COD. It cannot be decisively stated, however,
that the decreases in organic carbon was accompanied by an
increase in alkalinity, because the alkalinity was not mea-
sured routinely. If an actual loss in carbon occurred, and
if nitrogen and phosphate had remained constant while carbon
decreased, there would theoretically have been nearly suffi-
cient N and P to satisfy the carbonaceous algae growth poten-
tial of liquid entering the algae pond. Even though carbon
may have been lost, nitrogen as well as carbon and sulfate
was also lost as the carbon was passed through the anaerobic
system. The greatest loss occurred in nitrate-nitrogen. Losses
in this nitrogen form were as high as 90%. Losses in ammonia-
nitrogen also amounted to from 20% to 90% or more of that ori-
ginally introduced, depending on the time of year. Inasmuch
as there was so little nitrogen to begin with, proportional
losses in nitrogen kept pace with or exceeded losses in carbon,
with the result that a severe shortage of available nitrogen
prevailed throughout the series, i.e., in both the anaerobic
and the algae pond. Based on the results, the significant
conclusion is that it would be difficult to amplify the quan-
tity of nitrogen in the algae portion of the system by adding
nitrate or ammonia to the anaerobic pond because they are
apparently simply reduced or oxidized and emitted as nitrogen
gas or ammonia from the anaerobic pond and thus wasted. With
regard to the algae pond, N-fertilization is best accomplished
by adding nitrogen to the algae pond directly. The best ni-
trogen additive to the anaerobic pond probably would be or-
ganic N. Organic N addition is potentially provided by set-
tled algae brought in with recirculant and algae pond effluent.
When the applied BOD to the algae pond is 200 mg per liter,
10 to 15 mg per liter of NH3~N should be adequate to provide
for the nitrogen deficiency in the anaerobic pond effluent
going to the algae pond. Addition of the nitrogen as anhy-
drous ammonia probably is to be preferred to adding the nitro-
gen as nitrate since nitrate would be quickly reduced.
In the past, nitrate has been added to sour anaerobic ponds
90
-------
to provide some degree of odor control. However, because
of the large amount of nitrate which must be added to pro-
vide control (40% of the BOD) and its costs, this method
of controlling odors would be about 5 times as expensive
as would be control with floating surface aerators.
Phosphate added to the anaerobic pond and algae pond evi-
dently was accompanied by its rapid disappearance from the
systemprobably as a precipitate in the algae pond and
possibly by phosphate reduction in the anaerobic pond.
According to Waksman and Starkey (9), under anaerobic con-
ditions when organic matter and when phosphates and the
necessary bacteria are present, phosphates are reduced to
phosphate (B^PC^) , hypophosphites (I^PC^) , and phosphine
(PH3) gas with the release of C02- Thus, nitrates, sulfates,
and phosphates are all potentially reduced in anaerobic ponds.
Although the methodology of nutrient addition was not exhaus-
tively explored in this study, the prior discussion is
convincing evidence that the strategy of nutrient addition
is at least as important as the nutrient addition itself.
On the basis of the limited experience obtained in this study,
it is certain that nutrient addition could best be studied
in a full-scale system.
The question of why algal or facultative ponds following
anaerobic ponds and without filtration performed poorly in
BOD removal is explained on the basis of several facts de-
rived from the study. First of all, because of the effi-
ciency of BOD removal in the anaerobic pond, only a limited
amount of relatively stable BOD remained to be removed in
the secondary ponds. Secondly, nitrogen losses in the
anaerobic pond limited subsequent algae growth; and finally,
the presence of large amounts of colloidal suspended solids
in the algae and facultative pond effluent imparted to them
a BOD of about 100 mg per liter even when the loading was
very low. Had there been separation of suspended solids
from the final effluents from the secondary ponds of each
system, removals would have been greatly improved.
The greatest difficulties in this series of experiments
and in the entire study resulted from the fact that the pilot
plant was on a shunt from the main factory waste, and con-
sequently was subjected to very frequent failures in the
feed system. Inability to control this factor within the
budget provided for the study ultimately led to the termi-
nation of the studies, and to the conclusion by the authors
that any further pilot work with beet sugar wastes should
be done with the entire output of a factory rather than
with a shunt system.
91
-------
The fact that nitrogen and perhaps phosphate usually must
be added to flume water for aerobic treatment following
passage through an anaerobic pond, and the fact that federal
and local standards may be established regulating the quan-
tities of nitrogen and phosphorus which may be discharged
into the environment suggests that future studies must in-
volve the control of nutrient additions to give maximum
benefit with minimum residual discharge.
Control of effluent BOD as well as effluent nitrogen and
phosphorus will almost certainly involve a filtration,
coagulation, or separation step to remove suspended solids
from final effluents. The development of adequate filtra-
tion or harvesting systems is thus an area of significant
concern which must be further explored. Effective separation
following adequate treatment should permit significant reuse
of water for relatively high purposes within a factory.
Predators were extremely difficult to deal with in the algae
pond but it is not clear whether the same succession of pre-
dators would occur in an algae pond in which there was
sufficient nitrogen for algae growth, and hence, in which
carbon is limiting. Results obtained in recent studies of
domestic sewage systems give some evidence that certain
predators such as daphnia cannot withstand the pH changes
which occur in carbon-limited algae ponds. Because of their
relatively large physical size as compared to algae, pre-
dators can be removed from recycled streams by screening.
DSM or rotary screens having mesh openings about 200 to 400
microns are effective in predator removal. Both screening
and carbon limitation in preference to use of pesticides
should be further studied for predator control.
There is no clear explanation for the lack of methane fermen-
tation in the system studied, because as opposed to the find-
ings in this pilot study, methane fermentation is frequently
observed in primary beet waste ponds. General observations
indicate, however, that the fermentaiion is most active and
visible in those ponds which receive a substantial quantity
of mud. Whether this mud traps the gas and, hence causes
the release of larger and more spectacular bubbles, or whe-
ther it actually acts as an essential substrate surface for
methane bacteria is not clear. Because primary sedimentation
was used, little mud entered the anaerobic pond of this sys-
tem. Methane fermentation is always slow to start in new
systems. Yet there were periods during earlier runs of this
series when the ponds showed somp evidence of fermentation
more vigorous than that observed during the fall 1968 cam-
paign. Studies of a pond in which methane fermentation is
definitely established and in which the amount of settleable
solids introduced can be controlled would be required to
explore this phenomenon.
92
-------
The pertinence of these studies to cold climate installa-
tions should be considered. Chemical treatment with lime
for pH control and sedimentation with recycling water, and
discharge of excess water to an aerated-anaerobic pond is
the only alternative thus far explored (10) . This system
leads to accumulation of a high carbonaceous load in the
recycled water. The maintenance of a high pH causes pre-
cipitation and removal of essential nutrients for microbial
growth. Thus, decomposition in the anaerobic pond is slow
and unbalanced. It is believed that if covered digestion
ponds could be developed, it would be preferable to pass
wastes through an anaerobic pond prior to chemical treatment
Floating covers for the ponds would preserve factory heat,
prevent odors, and permit a high degree of fermentation to
occur. Following this fermentation, chemical treatment
with supplementary aeration could be applied, and superna-
tant liquids would be suitable for reuse in the factory or
for storage without odor nuisance. Thus, the development of
inexpensive pond covers would be a worthwhile study for
future investigation.
93
-------
-------
SECTION VII
ACKNOWLEDGMENTS
This research was supported by a demonstration grant WPD
93 from the Environmental Protection Agency and by matching
funds from the Beet Sugar Development Foundation.
Special thanks are due the personnel of Holly Sugar Company,
Tracy, California, for their interest, aid, and support
throughout the course of these studies.
We also wish to acknowledge the efforts of Mr. Henry Gee,
Research opecialist of the University of California, Berkeley,
for guiding the analytical work and preparing the figures
for publication.
We are also indebted to Mrs. Joan Montoya, Scientific
Secretary, for preparing the final manuscripts for this
publication.
We are especially grateful to the Welles Products Corporation,
Roscoe, Illinois, and to Mr, John Larson of the E. C. Cooley
Company, San Francisco, California, for furnishing the 5 H.P.
floating surface aerator used in these experiments.
95
-------
-------
SECTION VIII
REFERENCES
10
Beet Sugar Development Foundation, "Facultative and
Algal Ponds for Treating Beet Sugar Wastes", Report
on WPD 93-01-02 WPD 93-03 partial, Beet Sugar Develop-
ment Foundation, Fort Collins, Colorado (1967).
Tsugita, R. A., W. J. Oswald, R. C. Cooper, and C. G.
Golueke, "Treatment of Sugarbeet Flume Waste Water by
Lagooning - A Pilot Study", Journal of the American
Society of Sugar Beet Technologists, 15:4 282-297
(1969).
American Public Health Association, New York, Standard
Methods for the Examination of Water and Wastewater,
12 ed. (1967) .
Joint Industry/Government Task Force on Eutrophication,
P.O. Box 301, Grand Central Station, New York, N. Y.
10017, "Provisional Algal Assay Procedure", (1969).
Welles Products Corporation, Roscoe, Illinois, Bulletin
49 (1965).
Zabat, Mario, "Kinetics of Phosphate Utilization by
Algae", Ph.D. Dissertation, University of California,
Berkeley (1970).
Bronson, J. C., W. J. Oswald, C. G. Golueke, R. C.
Cooper, H. K. Gee, "Water Reclamation, Algal Production
and Methane Fermentation in Ponds", Journal Int. Air
Water Poll. 7:6-7 (1963).
Report of the Committee on Water Quality Criteria,
Federal Water Pollution Control Administration, U.S.
Dept. of Interior, Washington, D. C. (1968) .
Waksman, S. A., and R. L. Starkey, The Soil and the
Microbe, John Wiley and Sons, Inc., New York (1947).
Fischer, J. H., W. Newton II, R. W. Brenton, and S. M.
Morrison, Concentration of Sugarbeet Wastes for Economic
Treatment with Biological Systems, WPRD 43-01-67, Beet
Sugar Dev. Found., Fort Collins, Colorado (1968).
97
-------
OTHER REFERENCES
1. Walden, C. C., Water Use, Re-Use and Waste Water Dis-
posal Practices~in the Beet Sugar Industry of the UTTited
States and Canada, British Columbia Research Council,
Vancouver 8, B. C. (1965).
2. Ichikawa, K., C. G. Golueke, and W. J. Oswald, "Bio-
treatment of Steffen House Waste", Journal of A.S.S.B.T.
15, 2, 125-150 (1968).
3. Golueke, C. G., W. J. Oswald, and H. K. Gee, "Effect of
Nitrogen Additives on Algal Yield", Jour. Water Poll.
Cont. Fed. 30, 823-834 (1967).
98
-------
SECTION IX
GLOSSARY
algal centrifuged solids - algae removable by centrifuging
at 500 x gravity for 10 minutes.
campaign - (French) the period or periods of a year during
which the sugarbeet factory produces sugar.
flume water waste - the transporting and cleansing water for
sugarbeets prior to processing. The waste will be high
in suspended organic particles, soil, and dissolved
solids.
photosynthetic oxygenation - the net surface oxygen produc-
tion process from algae in aerobic ponds (gross photo-
synthesis less respiration).
Steffen waste - the waste from a process of treating molasses
to produce a precipitate containing sucrose which is then
treated to release free sucrose in solution. This waste
may or may not be discharged into the flume water.
99
-------
-------
SECTION X
APPENDICES
101
-------
APPENDIX A-l
9 -2
Visible Solar Energy Cal/cnr x 10
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Mean
Jul
2.83
2.83
Aug
2.58
3.24
2.88
2.22
2.83
-.
1.81
..
2.74
--
«
2.87
2.40
2.40
2.24
2.57
2.91
--
2.26
..
..
2.15
2.15
1.56
V
..
2.47
2.48
2.77
2.49
1.56
2.44
Sep
2.50
2.50
2.41
2.23
2.20
2.17
2.20
2.30
2.30
2.37
2.10
1.92
1.92
..
1.74
1.72
1.72
1.72
1.72
2.25
2.25
1.85
1.85
««
2.00
2.07
Oct
0.70
1.31
1.31
0.97
1.71
1.71
1.30
1.70
1.26
1.24
1.46
0.88
0.83
0.84
0.80
1.21
1.49
1.45
1.55
1.55
1.58
0.88
0.19
0.11
0.03
0.59
0.59
0.01
0.40
0.13
0.99
Nov
0.75
0.55
0.58
0.58
1.02
0.36
1.51
0.87
0.98
0.87
0.87
1.21
1.21
0.29
0.23
0.67
0.32
0.47
0.93
0.23
0.12
0.48
0.46
0.43
1.30
0.55
0.61
0.61
0.80
0.80
0.69
Dec
0.27
0.27
0.27
0.89
0.86
0.75
1.02
0.32
0.35
--
0.26
0.47
0.37
0.30
0.42
0.42
0.77
--
0.78
0.88
0.65
«
0.52
0.07
--
0.26
0.63
0.22
..
0.30
0.18
0.48
104
-------
APPENDIX A-2
Daily Minimum and Maximun Air Temperatures - Tracy
Degrees Farenheit
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
r*i
27
28
29
30
33,
Aug
Min
63
62
61
64
63
58
60
63
58
60
63
60
69
69
70
65
68
67
72
60
59
64
60
71
72
67
66
61
57
59
->c
yi
17
Max
98
95
100
98
96
92
96
96
92
96
102
102
104
105
104
102
106
107
103
95
99
99
99
98
100
99
96
34
96
100
91
98
37
Sep
Min
59
60
69
69
61
65
63
52
62
62
62
59
67
59
57
59
66
62
54
57
60
62
:;6
61
59
58
60
57
55
59
60
16
Max
93
96
94
93
90
95
88
85
89
88
88
95
95
92
90
82
80
86
89
95
90
81
'33
84
90
92
91
89
85
78
**»
89
32
Oct
Min
59
52
46
49
51
47
45
46
57
58
50
68
50
62
51
48
49
49
48
47
52
60
57
47
51
50
46
60
56
44
43
52
11
Max
75
80
73
77
72
78
82
85
89
86
87
8'J
88
84
81
86
87
88
84
83
73
77
78
79
81
79
81
75
77
78
81
81
27
Nov
Min
44
58
46
50
57
48
46
48
55
51
44
51
55
57
49
50
54
54
45
48
44
45
36
36
35
36
28
21
35
28
45
7
Max
84
81
81
71
68
74
77
74
69
74
67
66
62
71
68
74
77
68
62
66
70
67
57
56
61
61
61
51
57
55
..
68
20
Dec
Min
33
29
35
42
45
32
41
31
34
31
28
26
33
30
28
24
31
35
33
1
Max
56
58
50
65
58
52
56
56
55
57
52
53
48
50
53
47
50
50
54
12
105
-------
APPENDIX A-3
Waste Temperature and Surface Pond Temperature
Day
1
2
3
4
3
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
23
26
27
28
29
30
31
Av»
Aug
In*
35.5
33.5
«
-.
23
37
.*
«
29
38
..
34
34
__
36
37
31
..
..
..
36
35
36
._
..
33
35
An*
23
22
21
«
22
21
21
23
24
23
..
23
20
21
23
22
19
..
22
22
21
20
22
22
..
23
23
37 | 24
32 ' r:,
39 : 23
33 t 7.5
34.- 'V ' 22.2
Al*
21
20
20
20
20
20
24
23
22
..
20
18
19
20
20
20
«.
21
19
19
21
21
23
*.
21
22
22
22
25
24
21
Sep
In
..
33
34
33
-.
35
«
34
33
31
33
33
33
..
.
-*
23
-.
35
-..
-.
..
21
20
.*
20
33.0
An
22
24
23
23
23
23
*.
23
22
22
22
22
23
..
21
...
24.5
21
19
18
...
19
19
20
21
20
21
20
>
21.5
Al
23
21
21
21
22
22
«
20
19
20
20
21
22
»
20
25.0
20
16
17
»
19
19
20.5
21
20
20
18
20.3
Oct
In
32
32
26
»
«
31.7
31.1
32.2
38
..
33
..
31
--
30
..
31
30
..
34
35
33
»
35
33
32
32.1
An
17
17
18
17
21
17
--
22
15
16.7
1S.O
..
19
14
17
17
16
18
18
17
17
18
18
.-
19
16
15
15
17.2
Al
17
17
18
18
20
--
16
--
15
16
17.2
19.0
..
18
16
16
--
16
15
--
17
17
17
18
18
17
-.
18
16
16
15
16.2
Nov
In
30
--
--
-.
-_
29
28.5
29
..
..
..
._
*_
--
-.
..
-..
--
...
..
*.
*.
.-
22.5
*.
.-
*.
27.8
An
15
17
17
15
17
15.5
17.5
..
17
17
17
14
14
12
--
14
14
13.5
14.0
13.5
14
12.5
11.5
11.5
--
10
11
--
14.3
Al
15
__
15
16
17
15
14
18
«
15
16
13
13
10.5
10
14
14
14.5
13.5
13.5
13
«
12.0
12.0
9.5
-,
7
9
13.3
Dec
In
.-
--
«
30
28
--
29
32
30
25
27.5
30.0
.-
27.5
..
27.7
An
11
10
11.5
10
10
10
-.
12
12
12
9
9.6
13.0
10.5
12
11.0
Al
9
7
8.5
8
9
9
__
12
12.5
11
10.5
9.0
10.0
.-
10.0
9
9.6
*In
An = Anaerobic Al * Algae
-------
APPENDIX B
Flow Data
B-l July and August Flows
B-2 September and October Flows
B-3 November and December Flows
107
-------
APPENDIX B-1
Daily Flows in Gallons Per Minute
Day
**i/
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
July
Inf*
000
000
112
..
--
.-
000
125
132
61
Rec*
148
148
148
148
148
148
148
148
148
148
Trans*
.-
*<*
««
-.
..
»
««
>
<*
«
Eff*
--
**
..
mm
* m»
..
..
«M
..
--
AUg
Inf
132
132
132
..
000
000
000
000
152
152
...
152
152
152
152
152
152
..
000
000
152
152
152
000
..
000
152
152
152
152
152
105
Rec
148
148
148
« *
148
148
148
148
148
148
«*
148
148
148
148
148
148
..
148
148
148
148
148
148
«
148
148
148
148
148
148
148
Trans
«
--
..
000
000
000
000
150
150
<..
150
150
150
150
150
150
000
000
150
150
150
000
>
000
150
150
150
150
150
100
Eff
000
000
000
000
000
000
152
152
152
152
22
* Inf * Influent Rec = Recirculant Trans - Pond 1 effluent
Eff = Effluent from algae pond (see Figure 5)
108
-------
APPENDIX B-2
Daily Flows in Gallons Per Minute
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Sep
Inf*
-_
152
152
152
000
152
000
152
152
152
152
152
152
..
000
000
000
000
000
180
-.
000
000
000
000
000
000
-.
175
75
Rec*
»
148
148
148
148
148
148
--
148
148
148
148
148
148
-.
148
148
148
148
148
148
_.
148
148
148
148
148
148
»
148
«
148
Trans
_
--
..
..
190
220
90
...
205
250
250
250
260
260
_.
122
225
220
135
135
275
--
150
135
155
135
125
115
--
115
183
Eff*
_
052
045
40
40
35
32
-.
34
35
32
152
235
235
*»
92
172
108
170
148
75
--
75
75
75
75
75
75
....
75
90
Oct
Inf
215
250
000
000
150
..
000
163
170
170
163
153
_
170
000
145
153
000
170
..
225
203
000
160
192
122
*.
152
160
000
160
128
Rec
148
148
148
148
148
»
148
148
148
148
148
148
*.
148
148
148
148
148
148
._
148
148
148
148
148
148
«
148
148
148
148
148
Trans
190
220
165
125
115
190
165
190
165
190
115
*
190
115
220
190
193
193
*..
280
252
225
225
225
304
153
220
190
220
195
Eff
68
68
68
68
70
68
68
68
68
68
65
>«
70
60
68
67
67
75
«
78
78
72
72
100
100
_ m
100
100
100
100
76
Inf = Influent Rec = Recirculant Trans = Pond 1 effluent
Eff = Effluent from algae pond (see Figure 5)
109
-------
APPENDIX B-3
Daily Flows in Gallons Per Minute
T\ tfklfl
uay
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
26
29
30
31
Ave
Inf -
Nov
Inf*
122
100
000
000
000
067
040
067
..
000
000
000
000
000
000
..
000
000
000
000
000
000
..
000
000
30
!<
000
000
..
17
Rec*
148
148
«#
148
000
000
000
000
000
000
000
000
000
000
000
"«
000
000
000
000
000
000
»
052
075
000
>
000
000
w
23
Trans*
220
220
005
000
000
049
049
033
..
000
000
000
000
000
000
*
000
000
000
000
000
000
>
000
48
20
«
000
000
26
Eff*
100
100
<
100
90
90
83
83
183
..
000
000
000
000
000
000
>
000
000
000
000
000
000
»
000
000
000
000
000
..
33
Dec
Inf
mm
000
000
000
000
098
132
098
068
115
135
122
170
..
210
000
ftm
..
82
Rec
*
000
075
105
092
090
092
..
092
092
092
092
092
128
-.
105
000
<
..
82
Trans
i
000
000
048
000
168
170
M
138
138
198
131
151
220
<>
220
000
«
...
113
Eff
00
00
00
00
00
00
»
68
68
68
68
68
68
98
00
..
36
Influent Rec » Recirculant Trans » Pond 1 effluen
Eff - Effluent from algae pond (see Figure 5)
110
-------
APPENDIX C
C-l Unfiltered COD Values
C-2 Filtered COD Values
C-3 Unfiltered BOD Values
111
-------
APPENDIX C-l
Unfi Itered COD mg/1
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Aug
In*
1860
548
..
1525
1195
2884
1258
1440
1430
1590
1482
580
1696
1450
An*
274
347
240
342
355
320
484
364
475
466
475
420
491
389
Al*
232
258
213
253
271
275
315
238
382
365
462
398
427
314
Sep
In
2220
1499
321
1095
1439
1530
1890
1340
2670
2398
1699
1118
1053
1559
An
678
487
607
647
619
640
630
553
705
693
601
652
661
630
Al
596
462
610
498
512
536
561
503
553
566
532
610
532
544
Oct
In
908
865
1296
2373
1572
1710
2770
1270
1130
2920
1110
1066
1410
1570
An
665
665
780
745
754
825
762
613
818
860
732
876
693
750
Al
630
620
710
594
656
540
735
724
685
630
60S
766
620
656
Nov
In
1428
1307
1070
1540
3643
1130
2220
2060
2270
2458
2620
2183
1590
1960
An
595
802
813
723
764
785
705
642
708
610
683
788
674
715
Al
578
677
690
558
6?*
643
672
551
650
575
471
678
517
610
Dec
In
927
2800
1680
2240
2070
3060
3380
2308
An
672
690
608
655
597
788
1022
1053
759
Al
488
538
522
399
511
538
757
881
579
*In = Influent
An - Anaerobic
Al - Algae
-------
APPENDIX C-2
Filtered COD mg/1
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
In*
738
380
_.
..
1090
1100
825
1282
828
1473
1138
428
1293
961
An*
254
255
151
242
204
214
320
212
195
288
212
123
148
217
Al*
76
84
93
61
195
222
89
102
153
102
119
84
59
112
Sep
In
1018
1321
«
889
859
1240
1158
618
2350
_«
.-
..
-
..
1182
An
271
173
132
136
132
178
99
65
114
_-
'
--
144
Al
135
99
140
107
144
153
74
53
143
-.
--
«
116
Oct
In
730
665
687
2125
1262
685
2700
1150
980
1450
768
850
1285
1180
An
133
142
115
98
142
106
186
34
196
179
85
212
155
137
Al
124
115
89
98
133
62
18
34
77
153
212
138
104
Nov
In
1245
1210
1160
1500
1873
1036
1685
1340
1970
1380
2180
2100
1357
1541
An
139
228
337
295
218
280
209
234
125
125
128
272
127
209
Al
114
196
165
197
140
130
142
125
125
67
118
262
170
150
Dec
In
1241
2720
1700
1760
1740
2640
1980
1969
*In = Influent An = Anaerobic Al = Algae
An
177
126
141
113
133
179
289
165
Al
202
160
141
86
90
109
125
130
-------
APPENDIX C-3
Unfiltered Biochemical Oxygen Demand 5-Day 20°C,
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
In*
917
395
..
1070
743
1060
1110
1105
818
1238
943
1282
1120
985
An*
145
149
159
165
183
197
255
220
202
215
184
142
174
184
Al*
75
75
115
85
95
62
92
98
116
103
114
114
118
98
Sep
In
1016
1070
288
832
711
1270
842
990
1710
1040
588
478
390
863
An
155
149
190
237
173
232
202
204
237
216
65
75
39
167
Al
126
139
186
143
171
177
182
173
120
129
40
58
38
130
*In = Influent An = Anaerobic Al = AJ
Oct
In
510
450
330
980
540
645
845
510
516
688
675
360
1072
625
An
42
50
54
97
94
76
100
103
70
123
124
101
145
91
Al
20
35
35
63
50
68
67
49
66
67
67
65
76
56
Nov
In
880
1205
1100
980
970
885
690
574
1260
1200
1043
945
885
971
An
160
197
150
141
180
165
145
126
98
74
49
42
26
119
Al
70
107
94
65
51
60
33
26
29
33
52
56
37
55
Dec
In
787
1365
960
864
1120
1440
204
963
An
38
28
65
53
113
168
«
78
Al
30
40
70
43
53
61
109
58
gae
-------
APPENDIX D
Physical Characteristics
D-l pH
D-2 Dissolved Oxygen
D-3 Volatile Dissolved Solids
D-4 Dissolved Ash
D-5 Volatile Suspended Solids
D-6 Suspended Ash
D-7 Centrifuged Packed Solids Volumetric
D-8 Conductivity
D-9 Light Penetration
115
-------
APPENDIX D-l
PH
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Min
Max
Aug
In*
8.6
8.7
8.7
7.4
9.9
«
9.6
8.3
8.7
5.8
8.9
7.2
7.4
8.4
An*
7.6
7.5
7.7
7.6
7.7
7.6
7.6
7.8
7.4
7.5
7.1
7.7
7.5
7.4
7.5
6,9 I 7.6
8.8
8.3
8.8
11.4
6.7
7.9
7.8
7.7
7.4
7.7
7.4 j 7.7
7.1 1 7.8
7.7
9.3
7.3
6.9
5.8
11.4
7.8
7.9
8.0
7.7
7.1
8.0
Al*
8.4
8.2
8.1
8.0
8.0
7.6
7.9
8.2
8.1
8.1
8.1
8.1
8.0
8.2
7.9
8.1
8.2
7.9
8.4
8.5
8.7
8.4
8.1
8.8
8.1
8.1
8.7
7.6
8.8
Sep
In
8.4
6.9
9.6
9.0
6.9
7.4
6.6
7.1
7.2
7.3
7.3
6.8
7,1
7.7
6.9
6.9
5.7
6.2
6.6
6.7
6.8
7.1
7.2
7.3
7.7
5.7
9.6
An
8.0
8.0
7.9
8.0
8.1
8.0
7.9
8.0
7.8
7.3
7.3
7.6
7.9
7,9
7.4
8.1
8.1
8.0
7.9
8*3
8.1
8.2
8.3
8.2
8.1
7.3
8.3
Al
8.4
8.4
8.3
8.3
8.2
8.5
8.5
8.0
8.2
6.9
7.9
7.0
7.9
7.9
7.8
8.1
8.2
8.1
8.2
7.9
8.1
8.1
8.1
8.3
8.7
6.9
8.7
Get
In
6.8
7,4
7*3
7.0
7.1
7,4
9.2
7,2
7.9
8.1
6.8
7.5
11.5
11.2
7.3
6.8
6.6
7.0
10.6
11.2
9.2
8.2
8.5
6.7
8.1
10.6
8.7
6.6
11.5
An
8.1
8.4
8.2
8.2
8.2
8.2
8.5
7.6
7.6
7.4
7.5
7.4
7.9
8.3
7.7
7.7
7.6
7.7
8.4
8.5
8.0
7.8
7.5
7.7
7.9
8.8
7.8
7.4
8.0
Al
8.2
8.2
8.3
8.3
8.2
8.9
8.3
7.5
7.4
7.3
7.5
7.4
7.7
7.6
7.7
7.8
7.4
7.4
7.8
7.8
7.7
7.7
7.8
7.6
7.7
8.0
7.8
7.3
8.9
Nov
In
9.5
8.3
7.7
6.3
6.5
8.4
9.1
9.3
6.7
6.5
6.4
11.0
11.6
6.9
8.0
9.0
7.6
9.2
7.6
7.1
11.0
10.5
6.4
6.6
5.8
5.8
11.6
An
7.7
7.5
7.8
7.1
7.4
7.6
7.7
7.6
7.4
7.2
7.3
8.8
8.8
7,1
7.2
8.0
7.6
7.4
7.2
7.0
7.2
6.8
6.8
8.0
6.9
6.8
8.8
Al
7.7
7.6
7.4
7.7
7.5
7.8
7.7
7.5
7.4
7.1
7.7
8.4
8.4
7.2
7.0
8.0
7.2
7.8
7.6
7.8
7.0
7.0
7.0
8.1
7.1
7.0
8.4
Dec
In
6.0
7.6
11.0
7.6
6.0
7.6
6.0
6.0
6.0
6.8
6.0
6.8
6.4
11.0
6.0
11.0
An
6.8
6.8
6.0
6.0
7.0
6.4
6.8
6.4
6.4
6.4
6.4
7.0
6.4
6.4
6.4
6.0
7.0
Al
6.8
6.8
6.4
6.9
7.2
6.8
7.0
6.4
6.8
6.4
6.8
7.0
6.8
6.4
6.4
6.4
7.2
*In = Influent
An = Anaerobic
Al = Algae
-------
APPENDIX D-2
PM Dissolved Oxygen in Algal Pond, Mg/1
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
July
11.8
10.3
--
.-
..
15.7
10.6
12.1
Aug
_
...
-.
5.7
5.0
--
_-
15.0
8.1
..
9.0
3.2
--
7.6
3.8
11.0
-.
0.2
..
6.9
..
0.6
0.0
0.0
..
1.1
1.8
0.0
3.5
Sep
*>w
..
13.6
8.1
10.1
13.3
2.7
**
5.1
1.3
1.7
3.5
1.3
0.6
...
2.8
...
-,
2.0
2.5
0.0
..
0.0
0.0
..
0.0
0.0
--
..
0.1
3.1
Oct
0.0
1.0
3.3
4.2
8.8
«.
6.5
6.0
3.2
3.2
1.6
0.0
..
0.0
0.0
--
3.5
0.0
.-
-.
0.0
0.0
0.0
0.0
..
..
0.0
0.0
...
--
..
2.0
Nov
M
..
--
-.
..
..
-.
--
..
--
^M*
--
..
..
..
2.1
3.2
7.9
6.5
5.2
10.5
10.3
14.0
11.7
12.5
8.39
Dec
.-
12.9
12.9
12.1
10.6
..
6.4
6.4
1.6
1.6
...
1.0
..
..
..
0.0
4.6
117
-------
APPENDIX D-3
Volatile Dissolved Solids,
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Jul
Irf*
1070
880
975
An**
294
372
333
Al**
264
272
268
Alig
In
1186
1214
1890
550
2240
236
1752
1886
876
3900"
1378
1134
1078
1198
1908
1140
848
1788
158O
1682
_.
1120
1666
1472
1614
1416
1102
1358
L *"
340
402
468
..
502
196
402
236
504
578
334
608
«
536
--
418
360
«
1062
648
256
630
488
798
..
310
1158
440
330
760
752
520
Al
306
278
376
340
138
330
214
368
538
250
300
330
298
344
,,
898
394
216
508
314
708
..
292
1070
260
246
430
422
391
Sep
In
__
1304
1306
456
1146
352
1244
«
1012
1020
1030
1432
1360
488
..
832
1342
1124
1556
2000
1732
..
«
..
-.
_.
1150
An
0
460
510
458
492
438
548
494
392
550
428
372
502
288
618
576
486
470
492
-.
..
--
--
-.
477
Al
__
236
340
582
374
302
104
464
388
280
480
358
1208
~
574
350
512
424
490
470
-.
._
--
--
441
Oct
In
..
1050
864
718
710
~
848
1366
2018
1134
1580
998
1204
1526
1272
1042
986
812
822
1880
1590
1552
1376
1500
972
1348
1526
1802
1250
An
«
472
180
846
376
--
414
572
976
550
860
442
--
442
954
310
726
468
558
-,
416
730
820
744
604
638
768
684
500
752
608
Al
__
492
350
490
444
294
448
944
414
1190
406
_.
312
1042
308
564
454
464
412
506
694
594
500
448
--
634
522
388
406
528
Nov
In
1896
478
1608
1410
1254
1326
598
2562
2538
1252
1218
3228*
1592
1656
..
1550
2094
1214
2040
1462
1306
«
522
1794
1846
1394
1684
1513
An
924
516
..
596
450
600
533
492
596
,.
3328*
648
564
318
624
932
..
380
918
666
484
538
--
364
364
276
--
410
604
557
Al
800
1278
~.
442
366
452
450
408
678
..
770
398
364
390
374
784
_.
312
-,
650
404
344
394
-.
358
426
390
»
376
562
507
Dec
In
__
1698
3472
806
1654
1626
1920
1912
1836
2138
2052
2724
2622
--
3452
4964*
2142
An
_
942
528
240
580
300
616
«
520
424
524
678
662
526
2270*
1330
606
Al
>«
882
202
444
550
322
486
«
418
400
412
572
568
..
1180*
1016
52
CO
^Excluded from Ave*
**In = Influent An = Anaerobic
Al = Algae
-------
APPENDIX D-4
Dissolved Ash, Mg/1
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
In**
1046
1108
1346
..
886
1338
«
964
1120
2980
1008
1068
1114
1064
..
452
1072
1008
1020
1434
1212
_.-
1168
594
1092
1240
1010
766
1128
An**
984
1136
1108
-.
1040
1278
1168
1142
1102
1004
1226
572
1096
1134
1010
--
484
1078
1210
980
1158
788
-.
1176
372
1034
1156
678
938
1002
Al**
1158
1186
1172
1144
1324
1220
1136
1198
1050
1234
1244
1212
1148
1264
1124
.-
650
1338
1222
1032
1282
618
-.
1084
418
1178
1082
934
1030
1099
Scp
In
_
1288
466
352
1038
1004
998
--
1064
1154
1046
1234
1254
942
1222
1078
1128
1286
1778
1724
--
--
--
--
--
,,
,-
1118
An
_
1010
972
1028
968
1042
912
-,
964
1514
360
1016
500
546
870
940
1058
988
934
902
-_
--
--
--
--
,.
--
--
-.
-.
922
Al
1028
1024
854
1010
920
426
._
1010
1436
164
1042
1050
1092
--
1084
1254
1086
1030
1004
1084
._
»
-.
«
»
--
»
..
..
978
Oct
In
«_
1106
1146
778
994
-.
1020
726
700
948
620
1508
«
1066
1020
1132
764
1006
1044
--
1072
876
874
696
920
998
»
814
828
1226
1016
946
An
_
966
1262
920
1110
..
1046
776
426
626
568
988
--
956
416
1028
700
934
858
--
1010
826
552
778
756
810
--
724
698
924
824
831
Al
««
1046
1436
1048
984
-.
510
958
520
1058
444
962
1256
632
1140
956
1012
1044
1130
902
726
804
984
950
--
748
870
1022
1046
930
Nov
In
976
790
..
1106
1360
1352
1164
1146
536
._
892
1314
1332
4302*
1488
794
,.
1176
1316
1090
1260
1236
1314
__
2300
1564
1416
.-
1272
1072
1215
An
494
822
-.
842
1170
958
1020
982
936
_«
578
972
1014
1106
974
286
_
790
--
626
848
930
912
-.
1130
1070
1274
._
1024
820
898
Al
584
1030
»
992
1066
1036
1020
1054
858
-.*
716
1060
1090
1086
1028
600
._
1042
920
780
1006
1018
1018
._
1112
1044
1234
1072
842
935
In
968
1162
1528
1094
1046
1038
1072
1136
1138
1012
1000
1030
..
1592
996
1129
Dec
An
»
482
986
1190
878
1150
996
1008
728
998
926
1152
964
.-
394
492
.-
884
Al
536
1092
1234
846
1780
1120
1036
1140
1044
934
1070
634
..
456
440
-.
954
*Excluded from Ave*
**In = Influent An = Anaerobic Al = Algae
-------
APPENDIX D-5
Suspended" Volatile, Mg/1
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Jul
In*1*
105
2470*
105
An**
88
79
84
Al**
103
84
94
Aug
In
930
672
80
--
49
1385
119
148
83
82
66
243
179
43
._
130
207
120
265
94
177
104
174
204
70
144
247
241
An
103
92
97
90
60
60
71
69
61
..
76
91
94
_-
133
86
--
103
143
101
164
167
153
179
198
223
226
192
296
128
Al
121
115
118
--
120
105
86
38
129
143
--
96
139
132
193
183
115
.-
127
157
108
189
144
228
224
251
232
241
264
228
156
Sep
In
-V
148
416
185
3265*
94
451
262
256
191
354
541
121
118
250
376
325
189
271
--
-,
--
378
An
..
356
145
368
379
343
358
--
407
429
383
396
472
404
_-
359
396
414
360
433
396
__
..
..
--
376
Al
»
303
341
344
478
478
311
--
307
491
300
438
321
350
--
351
384
517
354
371
301
-,
--
..
374
Oct
In
223
146
122
69
117
265
239
187
242
227
138
98
243
337
417
211
--
133
231
424
268
223
78
«
178
163
242
240
199
An
350
411
375
362
«
286
358
446
426
444
406
457
436
481
491
552
385
521
489
534
560
559
474
559
460
469
469
452
Al
345
379
367
427
383
378
407
393
394
334
414
448
409
399
506
417
415
503
474
523
542
394
340
447
294
407
414
Nov
In
119
411
160
71
592
94
113
26
128
--
145
141
125
81
3
226
..
251
160
238
994
37
94
506
173
«
75
18
199
An
437
436
454
..
374
383
375
392
383
507
..
395
372
411
433
418
415
.-
458
439
426
409
406
428
--
427
320
_-
434
385
__
413
Al
449
146
418
423
449
427
409
416
51
--
438
437
380
454
331
399
--
464
424
385
398
373
317
..
319
364
«
297
243
--
369
Dec
In
--
68
149
56
95
439
208
..
406
428
850
448
318
327
--
576
259
327
An
--
415
440
409
252
94
440
--
492
586
539
471
510
605
_.
757
867
492
Al
..
285
359
314
282
307
328
--
379
403
404
481
429
480
519
573
395
to
o
*Exclud«d from Ave,
**In = Influent An
Anaerobic Al = Algae
-------
APPENDIX D-6
Suspended Ash, Mg/1
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
16
19
20
21
22
23
24
25
26
27
28
29
30
31
Mean
Jul
In**
148
6030*
VM
An**
5
33
19
Al**
12
29
20
Aug
In
__
846
79
._
..
_.
218
304
-_
148
3
190
398
68
56
318
269
-_
586
157
159
--
174
90
323
120
184
318
239
An
22
9
24
3
28
1
_-
13
11
35
--
0
22
..
24
32
28
0
30
48
--
41
41
75
,
40
23
40
16
39
6
25
Al
17
8
23
8
33
--
--
16
21
35
_.
2
30
..
22
17
28
15
30
29
..
21
0
39
«
68
22
36
55
31
67
27
Sep
In
136
244
260
1264
86
540
370
946
292
595
1098
86
87
423
689
669
129
466
..
»-
465
An
60
5
58
82
76
48
--
86
139
80
83
168
51
..
140
82
89
89
86
46
82
Al
57
94
81
149
144
39
46
124
56
103
74
57
--
48
93
158
102
85
62
.-
88
Oct
In
465
142
263
66
225
539
474
441
465
622
241
249
724
1044
949
502
29
451
1051
593
458
228
--
283
233
440
425
447
An
113
102
120
87
..
61
116
106
91
150
108
..
81
148
243
178
260
191
-.
211
211
255
265
248
148
100
161
175
106
155
Al
105
76
129
145
156
110
94
86
122
105
77
125
161
83
132
141
***
159
128
163
201
241
121
--
252
108
48
125
131
Nov
In
149
189
203
..
0
301
137
211
299
132
39
5
64
81
62
464
-_
482
237
272
--
42
200
..
1237
181
24
73
..
212
An
0
83
52
«
34
16
25
49
98
481
..
21
40
55
91
158
46
_.
46
36
68
53
78
50
..
51
199
-.
67
78
>-
79
Al
27
109
36
41
51
34
49
63
66
75
72
95
97
152
79
..
41
76
192
91
73
67
--
69
66
..
59
100
-_
75
Dec
In
--
68
116
0
110
754
576
_-
758
769
169
880
809
699
619
291
472
An
--
17
22
34
30
17
87
..
125
179
104
256
157
196
_
536
364
152
Al
__
51
32
59
66
26
76
-,
9
77
84
149
102
230
~-.
194
208
98
H1
ro
^Excluded from Mean
**In = Influent An = Anaerobic Al = Algae
-------
APPENDIX -D-7
Solids Packed Wet Voluae of Solids Mg Per Liter
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Mean
Aug
In**
5.0
2.7
0.3
0.5
17.5*
«
0.9
1.2
1.5
0.2
0.7
2.0
1.2
1.2
1.1
1.0
1.5
1.8
0.8
0.9
0.4
1.0
l.l
0.7
0.8
1.2
1.2
An**
0.6
0.75
0.70
1.4
0.5
0.5
0.7
0.4
0.5
1.0
0.5
1.0
0.5
1.2
1.7
0.7
2.0
1.5
1.5
1.7
1.8
1.0
1.0
0.7
1.8
0.8
1.0
1.0
Al*"
0.7
1.2
0.8
1.8
0.7
0.5
1.2
1.0
1.8
2.0
1.2
1.3
2.5
1.2
1.3
1.1
1.0
0.8
1.5
1.3
1.5
2.8
1.8
1.5
2.0
2.0
1.5
1.4
Sep
In
0.8
2.2
1.2
3.7
0.4
2.0
1.5
1.0
1.2
2.8
3.5
0.9
0.4
0.7
2.5
3.0
1.0
2.1
6.4
0.8
1.0
0.8
0.8
0.5
4.1
1.8
An
2.0
1.5
1.8
1.3
1.8
1.5
1.5
1.5
2.0
1.5
1.5
1.0
1.0
1.4
2.0
1.0
1.5
0.9
3.5
2.5
1.5
1.0
1.0
0.5
2.5
1.6
Al
2.5
2.3
1.7
3.5
3.6
2.5
3.8
4.5
2.5
4.5
4.0
2.7
2.5
2.5
4.0
1.2
2.3
3.5
3.0
2.0
2.0
2.0
1.8
1.2
1.5
2.7
Oct
In
2.8
1.8
1.2
1.5
0.4
1.0
1.8
1.9
1.7
1.8
2.0
1.5
1.0
2.4
3.5
3.6
2.5
1.0
2.0
3.6
1.8
1.5
0.8
2.5
1.5
1.8
1.5
1.9
An
2.5
2.0
2.0
2.5
1.5
1.5
0.8
0.8
1.5
1.2
1.5
1.5
2.0
4.0
1.5
1.0
1.0
1.5
1.2
2.5
2.0
5.6
0.6
2.0
1.5
5.0
1.0
1.9
Al
2.3
1.7
3.0
2.8
2.5
1.5
2.8
2.0
4.5
2.5
2.7
2.5
2.5
3.2
1.2
2.5
2.5
2.5
2.5
2.5
6,5
4.5
0.9
1.5
1.0
5.0
1.0
2.6
Nov
In
0.7
1.0
1.3
0,2
0.3
1.0
1.2
1.0
1.0
0.5
0.3
0,3
0.3
0.5
2.0
1.0
0.6
0.6
0.7
0.2
0.8
6.8
0.5
0.4
0.5
0.9
An
1.5
1.0
1.0
0.7
0.7
0.4
0.8
0.9
0.5
1.0
0.5
1.0
0.7
1.5
1.0
1.5
1.4
1*0
0.5
1.0
0.9
1.0
0.8
1.0
0.7
0.9
Al
1.4
1.2
1.0
1.0
1.0
0.6
0.9
1.5
1.0
1.0
0.6
0.5
0.5
1.0
1.4
1.5
2.0
2.0
1.5
2.5
0.3
3.0
2.5
5.0
2.5
1.5
Dec
In
0.3
0.5
0.3
0.5
2.9
1.5
3.2
3.1
3.0
3.0
2.5
2.7
5.5
1.2
2.2
An
1.0
1.0
0.5
0.4
0.5
1,6
0.5
0.5
0.8
5.0
1.0
2.5
4.0
4.0
4.0
1.8
Al
0.2
2.5
0.4
1.5
2.0
1.8
0.4
0.2
2.0
2.0
1.5
2.0
0.4
0.5
0.6
1.2
^Excluded from Mean
**In= Influent An = Anaerobic Al = Algae
-------
APPENDIX D-8
Specific Conductance Mlcromhos
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
"In =
Aug
In*
290
310
290
310
243
..
_.
250
352
320
301
400
350
370
400
»
380
410
430
389
290
305
..
280
330
370
272
275
373
332
Intiuen
An*
210
290
280
270
290
280
270
280
250
270
29i
310
290
310
300
360
300
330
335
302
282
*«.
280
285
290
289
284
273
289
Al*
390
300
260
250
280
270
280
270
253
270
289
290
270
300
310
..
285
290
300
320
298
295
..
300
280
300
299
293
285
289
Sep
In
310
280
405
420
325
340
..
320
330
305
240
300
300
._
320
310
270
250
172
180
..
280
300
285
270
310
240
285
293
An
300
280
310
330
290
295
..
300
312
295
290
320
310
-.
330
300
273
290
275
280
-.
310
285
300
285
300
260
275
294
Al
300
296
340
325
290
320
.-
300
296
290
265
295
290
..
290
280
249
270
260
250
«
280
270
290
270
275
290
285
287
Oct
In
280
325
350
370
270
-.
350
390
320
340
340
290
310
220
298
415
310
332
325
335
244
350
321
342
272
370
350
350
329
An
280
320
310
330
260
..
330
330
340
330
320
270
340
350
343
395
316
330
..
311
335
332
368
310
361
390
360
375
370
334
Al
270
310
290
290
280
350
340
340
340
310
315
320
350
335
332
290
310
--
282
329
299
320
303
340
355
350
360
355
321
Nov
In
340
320
350
320
295
342
365
372
350
345
320
90
123
245
--
280
219
235
218
275
230
200
230
410
«*
320
290
283
An
370
330
370
310
310
310
335
340
340
337
325
323
360
350
--
341
330
320
312
330
300
-_
320
390
380
«
360
310
337
Al
370
335
350
331
380
345
349
360
335
327
370
405
400
320
--
360
355
345
348
351
310
355
400
294
..
335
305
349
Dec
In
-.
320
283
170
270
400
405
--
370
380
410
445
423
420
278
275
346
An
»*
370
360
435
390
460
350
--
340
360
390
415
400
390
380
390
387
Al
--
390
405
385
400
290
370
380
360
385
400
405
395
380
450
384
t an = Anaerooic AJ. = Algae
-------
APPENDIX D-9
Light Penetration, cm
Day
1
2
3
4
3
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Awe
Aug
In**
64
24
26
138
40
_
__
64
42
..
40
...
62
42
48
62
..
60
32
42
66
76
60
»
52
52
50
52
38
48
55
An**
88
72
66
100
88
86
80
84
78
..
62
80
64
54
58
50
..
52
62
52
62
50
58
»
44
50
60
44
40
56
77
A1*J
78
64
64
62
63
84
88
64
72
.
62
80
72
50
46
56
58
60
62
56
62
52
«
48
50
50
46
42
52
61
Sep
In
w
70
36
60
24
62
42
._
44
46
50
34
26
44
»
58
44
44
24
42
34
6
48
50
46
50
80
«
22
.-
43
An
36
20
36
22
30
36
..
24
36
24
34
32
28
_-
28
38
28
24
28
30
..
4
30
26
26
30
40
..
32
..
28
Al
40
32
44
22
36
44
..
52
42
46
48
40
36
..
42
52
34
44
30
36
44
26
40
30
32
26
..
42
38
Oct
In
22
32
28
40
88
78
«
30
32
28
34
44
32
--
30
36
30
20
46
54
36
30
34
36
34
44
--
40
60
46
39
An
20
30
20
22
34
26
..
24
24
24
24
42
22
140*
34
32
24
28
32
--
34
28
32
28
24
20
-_
20
20
14
26
Al
30
36
20
18
34
24
..
22
28
28
24
56
24
--
26
38
42
42
28
34
«
42
32
36
28
34
20
-.
34
18
18
30
Nov
In
88
78
40
114
68
48
58
60
--
48
61
46
38
30
62
26
36
46
42
28
70
--
38
32
56
--
56
50
._
53
An
30
28
--
20
36
36
36
28
32
30
28
34
36
30
44
30
30
36
38
26
30
30
38
38
.-
30
30
32
Al
30
32
-
14
18
32
34
26
28
-.
34
32
36
32
34
36
32
30
40
36
30
36
32
40
38
-,-
50
48
33
Dec
In
<«
64
76
200*
72
30
22
--
30
30
26
38
32
28
«
10
16
--
36
An
_
32
42
36
38
32
30
«
28
30
24
32
26
26
-.
16
24
20
29
Al
*
40
40
30
38
34
38
30
34
34
34
30
32
20
24
24
32
*Excluded from
**In = Influent
An = Anaerobic Al = Algae
-------
APPENDIX E
Chemical Characteristics
E-l Magnesium
E-2 Calcium
E-3 Sulfate
E-4 Sulfide
E-5 Organoleptic Odor
125
-------
APPENDIX E-l
Magnesium Mg Per Liter
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Atig
In*
18
..
46
73
__
75
141
51
48
42
35
41
39
39
65
55
An*
9.1
«
54
54
49
24
^
48
23
51
53
34
70
56
56
38
44
Al*
8
65
60
57
82
60
43
60
61
42
50
56
57
51
54
Sep
In
52
69
41
35
25
75
69
25
52
56
39
32
--
48
An
46
29
53
48
26
29
44
48
40
42
52
46
..
42
Al
29
31
51
30
37
25
32
61
66
40
50
55
42
Oct
In
..
»
..
..
__
--
..
28
87
133
51
75
An
..
.-
»
__
..
»
»
..
52
85
76
84
75
Al
._
«
--
.-
--
..
44
78
73
80
69
Nov
In
72
48
55
18
41
28
65
86
43
38
121
46
58
55
An
30
47
42
33
28
17
74
90
72
97
93
28
45
54
Al
11
55
47
14
29
26
47
44
41
50
58
46
45
40
Dec
In
32
40
21
83
44
18
«
40
An
41
46
57
70
58
57
80
58
Al
49
31
50
49
53
51
48
47
10
en
*In = Influent
An = Anaerobic
Al * Algae
-------
APPENDIX E->2
Calcium Mg Per Liter
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Aw
Aug
In*
210
224
209
280
196
340
148
148
92
136
392
192
96
304
212
An*
174
104
118
134
118
190
126
164
108
119
155
134
112
108
132
133
Al*
179
80
106
124
102
124
114
148
118
103
148
104
78
46
66
103
Sep
In
196
160
134
194
260
172
226
202
242
186
256
288
201
An
111
115
85
64
96
98
82
78
82
85
78
84
--
81.0
Al
76
89
64
84
100
112
136
86
114
100
80
40
..
90.0
Oct
In
216
176
192
140
180
142
336
136
156
188
128
46
60
96
157
An
84
80
78
74
98
76
72
98
94
46
93
40
52
54
74
Al
82
90
89
72
90
20
60
86
102
44
97
43
48
46
69
Nov
In
80
216
172
304
220
1152*
276
92
124
296
76
226
216
191
An
92
150
130
118
130
155
58
54
50
128
40
128
98
102
Al
114
128
126
140
116
146
118
118
118
118
106
115
110
124
Dec
In
100
220
148
184
164
214
142
_
168
An
116
122
103
70
108
116
94
158
111
Al
108
124
104
104
122
128
166
156
127
*In = Influent
An = Anaerobic
Al = Algae
-------
APPENDIX fc-3
Sulfate Concentrations Mg Per
Liter
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Mean
Aiug
In*
128
146
256
--
1500*
153
212
220
224
296
290
257
326
309
235
' An**
95
95
110
135
81
64
54
25
8
115
114
51
283
67
93
Al**
256
270
173
71
234
69
107
84
61
127
124
46
90
100
130
Sep
In
294
240
623
285
250
278
242
216
253
231
138
158
267
An
49
43
105
81
40
.-
92
56
34
58
15
77
59
Al
87
109
49
46
25
12
33
97
64
63
77
113
65
Oct
In
16
208
171
231
254
1400*
140
244
247
240
100
149
174
229
185
An
25
59
53
82
48
146
18
15
76
92
97
96
43
23
62
Al
23
82
112
102
128
87
71
78
95
117
265
79
53
69
97
Nov
In
206
186
242
112
231
290
232
230
311
69
240
123
191
205
An
15
57
23
89
198
35
84
49
71
52
48
58
106
68
Al
40
66
31
87
165
120
130
69
123
138
107
124
94
100
Dec
In
49
194
232
230
97
253
46
158
An
35
71
74
110
79
45
69
Al
17
100
87
127
92
100
65
84
*Excluded from Mean
**In = Influent An = Anaerobic Al = Algae
-------
APPEND IX E-4
Dissolved SuIfides Mg Per Liter
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aiug
In*
0
0
0
0.2
0
-.
0
0
0
0
0
0
0
0
0.8
0
0
0
0
0
0
0
0
0
0
0
O.tt
An*
6.0
5.0
4.0
5.6
0.4
4.0
0.4
2.4
6.2
4.4
0.1
0
0.7
0.2
0.1
1.1
2.5
0.4
1.4
2.4
1.7
1.2
0.5
0.5
1.5
0.3
6.5
2.2
Al*
0
0
0
0
0
0.4
0
0
0.3
0.0
0
0
0
0
0
0
0
0.9
0
0
0
0
0
0
0
0
0
.06
Sep
In
0
0
0
0
0
0
0
0
0
0
0.3
0
0.7
0.2
0.8
0.1
0
0.4
0.2
0.25
0.1
3.5
0.0
0.2
0.2
0.3
An
0.8
0.6
0
0.2
0
0
0.2
0.2
0.1
0
0.2
0.3
0.2
0.15
0.12
0.25
0.20
0.35
0.4
0.4
0.3
1.5
0.3
0.15
0.2
0.28
Al
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0.0
0.0
Oct
In
0.2
0.2
0.3
0.4
0.7
0.4
0.2
0
0.2
0
0
0
0.2
0.1
0
0
.05
0
0
0
0
0
0
0.1
0
0.13
An
0.2
0.2
0.2
0.2
0
0.2
0.2
0.2
0.2
0.2
0.3
0.2
0.2
0.25
0.3
0.3
0.3
0.2
0.2
0.5
0.6
0.8
0.8
--
0.7
«.
0.4
0.32
Al
0
0
0
0
0
0
0.1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0.1
..
0
._
0
.01
Nov
In
->»
--
-.
0.1
0.1
0.2
0.2
0.3
0
0
0
0
..
0
.~
_.
..
-
--
.~
0.1
0.2
2.5
0.3
An
^^
w
0.8
0.7
0.3
0.6
0.7
1.3
1,6
0.3
0.3
._
0.3
..
..
..
...
_.
..
»
0.3
0.5
0.0
.59
Al
-------
APPENDIX E-5
Organoleptic Odor Levels
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
23
26
27
28
29
30
31
Ave
Aug
In*
8
6
6
8
8
«
..
8
6
8
4
8
6
6
6
16
16
10
4
18
10
8
6
6
8
12
6
7.3
Art*
20
20
15
8
6
8
15
6
12
12
24
12
12
18
16
18
18
12
16
16
24
20
12
12
16
12
12
14.5
Al*
4
10
15
4
4
6
10
4
6
10
6
1
6
1
6
1
1
15
3
6
3
6
3
3
1
16
3
5.7
Sep
In
15
8
6
4
6
6
6
8
6
18
8
6
8
8
8
6
8
12
8
8
10
10
30
8
6
9.3
An
12
12
16
12
12
12
12
12
12
12
16
18
16
12
8
12
16
12
6
6
6
6
8
15
4
11.4
Al
3
3
3
3
1
1
1
1
1
1
1
3
1
1
3
1
6
1
18
1
1
1
1
3
6
2.6
Oct
In
10
8
20
25
24
20
8
16
16
16
12
16
16
8
8
8
8
6
10
20
20
6
24
12
12
8
24
13.6
An
6
10
25
12
8
6
16
6
6
1
4
6
8
4
4
15
6
10
10
8
15
10
3
12
18
25
25
10.3
Al
1
9
9
9
1
6
6
3
6
1
1
6
1
1
6
1
1
1
1
I
6
6
3
3
10
12
1
4.1
Nov
In
12
12
18
24
20
15
20
20
18
8
18
2
16
15
4
10
8
8
8
18
10
6
12
15
13.1
An
20
20
15
4
18
30
24
24
8
18
8
16
8
4
16
10
«
16
10
12
8
8
8
8
15
13.1
Al
15
15
12
8
6
8
12
12
8
20
1
1
8
3
1
1
--
3
1
1
3
1
1
1
3
6.0
Dec
In
12
24
4
4
6
6
15
4
8
4
4
4
12
8
9
8.0
An
8
1
6
4
1
1
4
10
15
15
15
15
18
16
16
9.8
Al
3
1
1
1
1
1
3
1
1
1
1
1
8
6
12
2.8
* In" = Influent
An = Anaerobic
Al e Algae
-------
APPENDIX F
Nutrients - Nitrogen and Phosphorus
F-l Tabulation of Nitrate-N Values
F-2 Tabulation of Ammonia-N Values
F-3 Tabulation of Total N Values
F-4 Tabulation of Phosphate Data
131
-------
APPENDIX F-l
Nitrate Nitrogen Mg Per Liter
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
In*
4.9
5.6
4.5
0.1
1.5
1.8
3.0
2.2
3.2
1.2
1.3
7.6
1.7
2.97
An*
0.4
0.6
0.4
0.3
0.5
0.3
0.4
0.3
0.3
0.2
0.4
0.4
0.2
0.3
0.36
*IrT = Influent 3
Al*
0.5
0.9
0.3
0.3
0.8
0.4
0.3
0.2
0.4
0.5
0.2
0.3
0.3
0.5
0.42
Sep
In
1.8
2.8
1.9
3.2
1.0
0.6
1.0
1.4
1.6
1.6
0.2
0.3
1.45
An
0.4
0.3
0.4
0.4
0.5
0.4
0.3
0.3
0.4
0.7
0.4
0.6
0.42
n = Anaerobic /
Al
0.4
0.4
0.3
0.3
0.4
0.3
0.3
0.7
0.3
0.6
0.3
0.5
0.40
Oct
In
2.3
4.3
0.5
3.8
1.2
0.1
3.1
1.6
0.4
7.8
3.6
4.3
3.8
8.0
3.2
An
0.8
0.9
0.4
0.2
0.5
0.4
0.5
0.4
0.5
0.4
0.4
0.4
0.6
0.7
0.51
Al
1.2
0.9
0.4
0.2
0.4
0.3
0.1
0.3
0.7
0.6
0.5
0.4
0.5
0.5
0.50
Nov
In
3.8
0.5
5.0
5.7
0.7
6.8
5.8
5.1
7.1
0.5
9.8
4.8
0.5
4.31
An
0.3
0.1
0.3
0.3
0.4
0.3
0.5
0.3
0.4
0.5
0.9
1.3
0.6
0.48
Al
0.2
0.1
0.3
0.7
0.4
0.2
0.5
0.4
0.5
0.7
0.8
1.3
1.0
0.55
Dec
In
0.8
5.4
3.8
1.9
3.4
1.7
5.0
3.14
An
0.2
0.5
0.4
0.5
0.5
0.3
0.4
0.8
0.45
Al
0.7
1.0
0.9
0.4
0.7
0.8
0.3
0.6
0.67
LL = Algae
OJ
to
-------
APPENDIX F-2
Ammonia Nitrogen Mg Per Liter
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
In*
1.9
1.6
1.5
--
1.4
2.1
1.3
2.4
1.3
1.0
1.4
1.2
1.1
3.1
1.64
An*
0.5
0.7
1.4
1.9
0.9
2.3
1.0
1.6
1.1
1.2
0.6
0.5
1.1
1.8
1.18
Al*
0.3
0.1
0.5
1.2
0.2
2.1
0.3
1.2
0.7
0.7
0.0
0.5
0.3
1.5
0.68
Sep | Oct
In
1.1
1.1
1.2
1.3
1.5
1.8
1.7
1.4
0.9
0.2
1.4
1.6
1.17
An
0.9
0.7
0.5
0.6
0.7
1.3
0.5
0.5
0.3
0.1
0.5
0.4
0.58
Al
0.3
0.4
0.0
0.2
0.6
0.5
0.2
0.5
0.0
0.0
0.7
0.2
0.30
In
Oo5
1.6
1.8
1.5
1.4
1.4
1.8
1.1
0.7
1.4
1.8
2.3
0.9
1.2
1.38
An
2.5
1.1
0.0
0.7
1.0
0.0
0.4
0.6
0.2
0.9
0.5
1.4
0.7
1.1
0.79
Al
0.9
0.4
0.0
0.3
0.9
0.0
0.9
0.3
0.2
0.7
0.4
1.1
0.9
0.5
0.54
Nov
In
2.1
1.2
2.5
1.7
3.5
1.0
5.4
1.5
1.8
5.3
1.6
4.8
3.5
2.76
An
2.9
1.4
1.1
1.7
2.1
1.5
1.1
1.7
1.6
1.1
1.8
1.3
1.9
1.63
Al
3.3
0.9
0.9
0.7
0.9
1.6
1.2
1.2
0.5
0.6
1.8
1.3
2.1
1.31
Dec
In
2.2
1.8
1.4
1.6
1.4
1.2
1.2
--
1.54
An
1.5
1.4
1.4
1.1
1.8
0.7
1.6
0.9
1.30
Al
1.7
1.9
1.2
1.3
1.1
0.4
0.5
0.7
1.10
*In = Influent
An = Anaerobic
Al = Algae
-------
Total
APPENDIX F-3
Nitrogen, Mg/1 as N
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Aw
Aug
In *
7.1
8.3
9.5
»
3.5
3.1
4.0
6.2
3.4
5.6
6.8
3.9
7.3
4.2
5.6
Art*
2.0
1.6
1.8
2.9
2.0
3.1
1.9
2.0
2.5
2.7
3.7
2.7
2.9
4.2
2.6
Al*
1.5
1.4
1.0
2.3
1.8
3.2
1.9
1.6
1.5
2.0
3.6
1.8
1.7
0.0
1.81
Sap
In
3.6
4.5
6.6
4.6
8.3
4.9
4.7
3.2
5.7
7.7
2.1
2.4
4.85
An
3.3
3.3
4.1
3.8
4.7
4.6
4.9
1.1
4.1
4.5
3.5
3.5
3.78
Al
2.8
3.6
4.1
3.6
4.8
4.3
3.3
1.7
4.6
11.2
3.9
2.7
4.23
Oct
In
3.2
6.0
4.3
3.9
2.9
5.6
4.6
3.3
3.5
6.0
6.3
4.2
5.3
7.7
4.77
An
4.2
2.2
3.3
3.9
3.0
3.4
4.9
4.6
3.5
4.1
4.9
4.3
4.9
3.6
4.22
Al
4.2
4.3
3.7
4.0
4.3
3.0
4.6
3.9
4.2
5.0
5.3
5.5
3.8
4.5
4.30
Nov
In
3.6
10.5
8.1
9.5
8.8
15.1
10.2
8.8
10.5
7.4
9.8
10.1
8.1
9.28
An
3.9
5.6
5.8
5.6
7.3
6.6
5.3
7.4
5.6
6.0
8.3
7.1
6.3
6.21
Al
3.8
4.9
2.5
5.6
8.4
6.0
5.3
6.0
5.9
5.3
6.4
6.9
3.9
5.44
Dec
In
7.1
6.4
6.9
7.1
10.7
5.6
8.8
7.53
An
6.0
5.6
5.6
6.5
4.2
5.9
5.6
6.7
5.77
Al
5.3
11.0
4.8
7.7
6.4
5.6
5.3
3.9
6.25
*In = Influent
An = Anaerobic
Al = Algae
-------
APPENDIX P-4
Soluble Phosphate Mg Per Liter as P
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
In *
3.3
2.8
3.5
..
1.9
0.9
0.5
0.9
0.5
0.9
0.5
2.4
0.3
1.5
An *
4.0
5.1
6.4
10.8
20.5
26.9
25.7
23.6
20.4
16.0
10.7
10.1
5.9
8.8
13.9
Al *
2.5
2.2
2.0
5.4
7.6
11.1
15.0
13.2
17.8
11.2
4.7
2.5
2.9
4.1
7.3
Sep
In
0.5
0.3
0.7
0
1.1
0.2
1.3
0.4
0.6
0.5
2.2
0.2
2.2
.78
An
0.5
0.6
0.8
0
0.1
0.0
6.1
0.7
0.3
4.8
10.2
0.6
1.8
2.04
Al
1.4
0.5
0.2
0
0.3
2.0
1.1
1.6
0.4
3.1
6.1
0.3
3.2
1.57
Oct
In
0.2
3.0
0.1
0.0
0.0
1.0
0.5
0.1
0.8
3.1
0.4
0.4
0.6
0.79
An
2.2
3.1
0.04
5.8
0.0
0.6
0.2
0.4
1.4
0.7
0.7
0.3
0.4
1.25
Al
3.0
0
0.2
.03
0.4
0.6
0.1
0.2
1.1
0.6
0.1
0.2
0.2
.54
Nov
In
1.4
4.5
4.8
0.1
0.6
0.1
0.0
1.2
1.0
1.9
0.4
0.9
3.5
1.53
An
0.8
4.3
8.6
0.0
0.9
2.4
0.1
0.2
0.1
0.5
0.4
0.1
0.2
1.43
Al
0.3
0.1
10.1
3.0
2.8
1.0
2.8
9.1
11.5
17.6
25.2
14.3
22.5
9.3
Dec
In
0.4
0.5
0.1
0.4
1.7
0.9
0.0
.*
0.57
An
1.0
0.4
0.2
0.5
0.4
0.3
0.1
0.5
0.43
Al
22.1
19.0
12.9
0.5
0.6
0.2
0.7
0.4
7.1
UJ
(Jl
*In = Influent
An = Anaerobic
Al = Algae
-------
APPENDIX G
Microbiological Activity
G-l Daily Algal Cell Counts
G-2 Daily Algal Cell Packed Volume
G-3 Count and/or Incidence of Daphnia
G-4 Count and/or Incidence of Rotifers
G-5 Count and/or Incidence of Purple Sulfur Bacteria
G-6 Gas Emission
136
-------
APPENDIX G-l
Algal Counts Cells Per ml x 10
-6
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Mean
Aug
An *
.140
.195
.170
.111
.162
.175
.420
.500
.067
.067
.042
.190
.150
.120
.095
.260
.480
.270
.112
.330
.500
.400
.366
.250
.300
.235
Al*
.385
.325
.370
.300
.400
.250
.580
.780
.242
.475
.425
.750
.810
.820
.215
.760
.620
.870
.870
1.17
2.22
1.40
1.04
0.85
0.76
.645
Sep
An
.347
.320
.300
,200
.102
1.90
.395
.440
0392
.250
.785
.420
.310
.300
.220
.230
.840
.400
.172
.160
.115
.480
.700
.425
Al
.448
1.70
1.50
1.89
2.78*
3.30
.935
2.30*
2.10
1.07
2.12
1.02
.750
.630
.730
.560
1.110
0.77
0.87
0.53
0.66
0.62
0.740
1.266
Oct
An
.137
.495
.190
.537
.410
.710
.380
.447
.600
.635
.315
.587
.445
.637
.630
.400
.275
.190
.760
.695
.295
.430
.377
.767
.660
.192
0200
.459
Al
.900
.855
.600
.877
1.28
.895
1.10
.735
.910
.840
.400
.657
.735
.907
.775
.4??
,7e_.
.7^-0
.907
1.02
,630
.680
.583
.872
,740
.412
.375
.766
Nov
An
.680
.940
.300
.695
.72
.22
.177
.500
,742
.966
.210
.710
.270
.600
,320
.230
.490
.507
.310
.100
.310
,250
.372
.475
.050
.444
Al:
.867
1.10
.400
.750
.175
.30
.170
.520
.860
1.50
.580
.922
.720
1.09
.860
.904
1.02
1.03
1.003
2.50
1.20
2.12
1.48
1.31
0.97
.974
Dec
An
.220
.396
.38
.540
.636
.163
.600
.686
.630
.583
.200
.150
.170
.200
.163
.382
Al
2.19
1.67
1.31
1.72
1.75
2.40
.980
.990
.985
.916
.528
.510
.470
.410
,340
1.001
*An = Anaerobic pond effluent
Al = Algae pond effluent
137
-------
APPENDIX G-2
Algal Solids Packed Vet Volume Mg/L
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
An*
.42
.45
.63
.70
.35
.35
.35
*24
.25
.60
.15
.40
,10
,48
.51
.14
,70
,52
,45
.68
.54
,25
.30
.21
,54
,24
,25
,40
Al*
.59
1.08
0.72
1*62
.56
.47
1.08
.90
1.71
1.9
1.14
0.97
1.25
.90
1.17
.99
.90
.60
1.42
1,17
1.35
2,1
1.62
1.35
1,80
1.90
1,35
1.20
Sep
An
.5
.45
1.26
0.78
1,08
0.60
0.60
,75
,80
1.05
.25
.30
.65
.84
1.1
0.6
,75
.27
.87
.75
0.5
0.8
0.4
,23
.62
.67
Al
2.25
2.07
1.44
2.45
3.24
2.35
2.85
3.60
1,87
3.60
3020
2.16
2.00
2.00
2.6
.24
1.49
2.10
1.80
1.1
1.3
1,6
1,62
0,84
.75
2.02
Oct
An
.62
.60
.5
.6
.6
,45
.20
.16
.37
.24
.75
.45
.40
1.2
.37
.25
.10
.30
.60
.25
.20
1.0
.21
.12
.15
.5
.2
.420
Al
1.84
1.20
2.40
2.52
1.87
1.03
2.10
1.50
4.3
2,0
2.28
1.75
1.30
2,56
0.60
1.25
1,25
1.70
1,75
1.50
3.25
2.40
0,76
.60
.45
1.5
.70
1.69
Nov
An
1.03
.6
.85
.56
.66
,36
,60
.27
,40
,80
.45
,73
.56
,75
.85
1.12
1.26
0,40
0,42
0,90
.61
,55
.24
0,6
,35
,64
Al
.56
,96
,90
.90
.80
.57
,90
1.20
.60
.85
.42
,42
.45
.60
.84
0.60
1.20
1.80
0.42
2.23
.25
2.85
2.10
4,5
2.25
1,17
Dec
An
,25
.28
.24
.12
.35
.48
.35
.15
.64
1,7
.33
.94
2.2
2.4
2.4
0.85
Al
.16
2,25
.27
1.2
1.9
1.62
.38
.18
1.90
1.6
1.35
1.5
0.4
0.45
0.56
1,05
*An - Anaerobic pond effluent
Al " Algae pond effluent
138
-------
APPENDIX G-3
Daphnia, Organisms Per Ml
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Aug
An**
+
+
+
*
*
+
+
+
+
Al**
*
+
+
+
+
20
+
+
+
+
Sep
An
2.5
Al
+
7
Oct
An
+
Al
.+
Nov
An
Al
Dec
An
Al
^Indicates presence in sample but not enumerated
**An = Anaerobic pond effluent Al = Algae pond effluent
139
-------
APPENDIX G-4
Rotifera Cells Per Ml x 10
-6
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
23
26
27
28
29
30
31
Mean
Aug
An*
--
Al*
Sep
An
,02
.122
,002
,005
.012
.002
-_
..
.-
.007
..
.005
..
.000
..
._
-.
..
.019
Al
.037
.004
.012
.062
.060
.035
.022
.092
.045
.010
.012
_.
-.
.040
.012
.013
TNC
«._
-.
*"" i
.393
__
.032
Oct
An
_ m
.012
.000
.005
« 4
***
.000
...
.022
.020
.030
.000
.000
.000
.025
.040
.045
mm
-.
-.
* v
.040
.043
.027
..
-
.022
.175
.001
...
.027
Al
mm
.000
.000
.042
..
..
.020
.025
.020
.090
.125
.000
.000
.035
.090
.117
.070
-.
..
--
«
.060
.065
.028
«
_
.025
.010
.
_,
.043
Nov
An
-
..
«
000
--
-.
--
..
..
-_
..
..
--
.-
..
..
..
..
-.
..
~_
._
--
__
..
-.
II
mm
mm
».
000
Al
--
mm
1
.300
..
_.
k M
_.
mm
mm
mm
mm
mm
mm
mm
mm
mm
mm
.005
mm
.040
.020
..
._
mm
mm
w
-~
..
B
__
.022
Dec
An
mm
mm
mm
mm
000
..
IHM
--
--
..
mm
mm
mm
mm
000
Al
mm
mm
-_
000
..
__
..
--
..
..
_
*
__
000
Values excluded from mean
*An » anaerobic pond effluent
Al = algae pond effluent
140
-------
APPENDIX G-5
Purple Sulfur Bacteria Cells Ml x 10
-6
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
Aug
An*
Al*
Sep
An
*
.407
.020
*
0.430
3.76
+
0.86
+
51.6
6.4
3.44
3.01
10.32
36.5
+
10.61
Al
+
*
2.58
2.58
Oct
An
3.87
0.86
0.00
1.29
+
3.01
0.40
1.57
Al
+
+
0.00
+
000
Nov
An
+
f
--
Al
+
+
+
+
--
Dec
An
Al
*An = Anaerobic pond effluent
Al = Algae pond effluent
141
-------
APPENDIX G-6
Gas Emission From Anaerobic Pond As Measured by
Bronson1 Collector and Wet Meter (liters/day)
Day
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
Ave
July
<
mm
Aug
_
mm
mm
mm
0.90
0.70
1.56
1.06
1.70
--
-.
1.71
1.71
1.71
1.50
1.55
mm
mm
1.50
1.50
0.90
1.10
--
mm
0.28
2.33
0.96
1.77
1.83
--
1.38
Sep
mm
1.51
1.65
4.32
1.38
1.28
»
..
1.11
0.98
1.40
1.12
0.63
mm
mm
it
ft
*
ft
ft
mm
mm
ft
ft
ft
ft
*
IB"
*
ft
mm
1.54
Oct
ft
ft
ft
*
..
>
ft
ft
*
ft
3.10
mm
mm
1.97
1.97
2.15
2.04
0.98
mm
mm
2.20
1.87
0.05
0.09
1.10
mm
mm
0.03
1.14
1.14
1.14
1.42
Nov
0.62
mm
..
0.50
1.05
0.76
0.86
1.43
*-.
mm
0.86
0.47
0.49
0.02
0.04
mm
mm
0.02
0.04
0.01
0.01
0.01
..
0.01
0.01
0.00
mm
0.01
mm
mm
0.36
Dec
mm
0.01
0.00
0.00
0.10
0.0
mm
mm
0.0
0.1
0.1
0.2
0.0
..
0.0
0.05
*Wet Meter Inoperative
Collector Constant!
To convert liters per collector day
to cubic feet per acre per day,
multiply by 171,
142
-------
APPENDIX H
Algal Species Occurrence
H-l August Anaerobic Pond
H-2 September Anaerobic Pond
H-3 October Anaerobic Pond
H-4 November Anaerobic Pond
H-5 December Anaerobic Pon4
H-6 August Algal Pond
H-7 September Algal Pond
H-8 Octobet Algal Pond
H-9 November Algal Pond
H-10 December Algal Pond
143
-------
APPENDIX H-l
August - Anaerobic Pond - Algal Species Occurrence
Algal Species
Oa/*1 1 1 «t~rtt*l A
VaWA 4. xtt^v& *H
*5 ***vti Art A oim i e
d Wvl Ms UV S»IUUo
Chlorococcum
N1 t»rfi 1 A
ii x w &CX1 x et
(Tl 1 At*A 1 1 B
lull XwfQ X Xo
Eturldnn
£fUJ£ X VILA
FhACtie
&£KCi.%^«dA
Fragllaria
Anabaena
Pyrobotrys
St igeoc Ionium
Actinastrum
Coe lastrum
Cy clot el la
Tetraedron
Closterium
Ank i s tr ode sinus
Se lenastrum
Anabaenopsis
Navlcula
Chlorococconeis
Vocystis
Microspora
Gomphos phaer i a
Microcystls
Ste phanod 1 s cus
Falmella
Gomphonema
Staurastrum
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 31 NO %
+ * 2 7
+ + 27
+ + + + + + 8 30
+ + + + + ++ 7 26
-------
APPENDIX H-2
September - Anaerobic Pond Algal Species Occurrence
Algal Species
Oscillatorla
Scenedesmus
Ch lorococcum
Nitzchia
Chlorella
Euglena
Phacus
Fragilaria
Anabaena
Pyrobotrys
Stigeoclonium
Actinastrum
Coe lastrum
Cyclotella
Tetraedron
Closterium
Ankistrodesmus
Se lenastrum
Anabaenopsis
Navicula
Ch lor ococcone i s
Oocystis
Microspora
Gomphosphacria
Microcystis
Stephanodiscus
Palraella
Gomphoneraa
Staurastrum
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 31 No.
j j.jj AAA ^ ^ j. ^ A A 4i A A 17
+ * * * * + 6
A
+ + 2
+ 1
* I
+ + * + 4
* + + 3
+ 1
+ I
f + + + 4
+ ***++*+ 8
%
87
77
96
96
* \J
73
/ rf
27
36
^U
55
5
5
18
14
5
5
18
36
t_n
-------
APPENDIX H-3
October - Anaerobic Pond Algal Species Occurrence
Algal Species
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 31 No.
Osclllatorla
Scenedesnus
Chlorococcum
Nitzchia
Euglena
Phacus
Frag liar la
Anabaena
Pyrobotrys
StIgeocconlum
Actinastrum
Coelastrum
Cyclotella
Tfttraedron
Closterium
Ank i strodesmus
Selenastrum
Anabaenopsis
Diatoma
Ch lor ococcone i s
Oocystis
Microspora
Gomphosphaer i a
Microcystis
Sephanodiscus
Palme1la
Gomphonema
Staurastrum
+ + + + + +
+
+ + + +
+ + +
+
+ + 12 86
9 64
+ + 13 93
+ + 13 93
+ 9 64
4 29
+ + 10 71
1 7
1 7
+ + 4 29
I 7
-------
APPENDIX H-4
November - Anaerobic Pond Algal Species Occurrence
Algal Species
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 31 No. %
Oscillateria
Scenedesmus
Chlorococcum
Nitachia
Ch lore1la
Euglenj?
Phacus
Pragilaria
Anabaena
Pyrobotrys
Stigeoclonium
Actinastrum
Coelastnuc
Cyc lot el la
Tetraedron
Closterlum
Ankistrodesraus
Selenastrum
Anabaenopsis
Navicula
Ch lorococcone i s
Oocystis
Microspora
Gomphosphaeria
Mlcrocystls
Stephanodiscus
Palmella
Gomphoneme
Staurastrum
50
50
8 80
10 100
4 40
2 20
1 10
1 10
-------
APPENDIX H-5
December - Anaerobic Fond Algal Species Occurrence
Algal Species
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 31 No.
CO
Oscillatoria
Scenedesmus
Chlorococcum
Nittchia
Ch lor el la
Euglena
Phacus
Fragilaria
Anabaena
Pyrobotrys
StigeocIonium
Act inas trust
Coe las trust
Cyclotella
Tetraedron
Closterlum
Ankistrodesmus
Selenastrum
Anabaenopsis
Navicula
Ch lorococconeis
Oocystis
Microspora
Gomphos phaer i a
Microcystis
Stephanodiscus
Falmella
Gomphonema
Staurastrum
3 100
I 33
1 33
2 67
1 33
33
1 33
1 33
-------
APPENDIX H-6
August - Algal Pond - Algal Species Occurrence
Scenedesmus
Chlorococcum
Nitzchia
Qtlorella
Phacus
PC ag liar I a
Anabaena
.Pyrobotrys
Stigeocloniusa
Actlnastrum
Coelastrum
Cyclotella
Te.traedron
Closterium
Ankistrodesraus
Selenastrum
Anabaenopsis
Diatoma
Chlorococconeis
Oocystis
Microspora
Gomphosphaeria
Microcystis
Ste phanod i s cus
Palme 1 la
Gomphonema
Staurastrum
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 31 No.
+ + + 3
+ 1
+ +++ ++ + 7
+ -f + + ++ + 7
+ +2
%
8?
11
67
4
26
26
7
-------
APPENDIX H-9
November - Algal Fond Algal Species Occurrence
Algal Species
Oscillatorla
Scenede sinus
Ch lorococcum
Nitzchia
Chlorella
Euglena
Phacus
Fragilarla
Anabaena
Pyrobotrys
Stigeoc Ionium
Act inastrum
Coelastrum
Cy clot el la
Xetraedron
Clbsteriiuo
Ankistrodesmus
Se lenastrum
Anabaenopsis
Diatoma
Ch lor ococcone i s
Oocystis
Microspora
Gomptios phaer i a
Microcystls
Stephanodiscus
Palme 1 la
Gomphonema
Staurastrum
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 No. %
+ + * + + + 6
+ + + + + + « +8
+ + + +4
+ + + + 1- 4> + + +9
+ + + + ++ + + + +10
-C + +++ + + + 8
+ + + 3
+ + + 3
+ 1
+ * +3
+ 1
60
80
40
90
100
80
30
30
10
30
10
to
-------
APPENDIX H-10
December - Algal Pond Algal Species Occurrence
Algal Species
Oscillator! a
Scenedesmus
Ch lorococcum
Mtzchia
Chlorella
Euglena
Phacus
Fragilarla
Anabaena
Pyrobotrys
Stigeoclonlum
Actinastrum
Coelastrum
Cyclotella
Tetraedron
Closterium
Ank i strodesmus
Se lenastrum
Anabaenopsis
Diatoma
Ch lor ococcone i s
Oocystis
Microspora
Gomphos phaer 1 a
Mlcrocystis
Stephanodiscus
Pa Intel la
Gomphonema
Staurastrum
Day
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22 23 24 25 26 27 28 29 30 31 No. %
+ + + 3 60
+ + + + 4 80
+ + + * ' 4 80
+ + + + 4 80
+ + 4 80
+ + + 3 60
+ * 2 40
* 1 20
* 1 20
+ 1 20
H
Ul
U)
-------
-------
OSD
-SELECTED WATER
RESOURCES ABSTRACTS
INPUT TRANSACTION FORM
1. Report No,
4. Title
ANAEROBIC - AEROBIC PONDS FOR
BEET SUGAR WASTE TREATMENT
7. Author(s) Oswald, William J.» Tsugita, Ronald A.,
Golueke, Clarence G., and Cooper, Robert C.
9, Organization
Beet Sugar Development Foundation
P. 0. Box 538
Fort Collins, Colorado 80521
12. Sponsoring Organization^^ _
15. Supplementary Notes
Environmental Protection Agency report
number, EPA-R2-73-025, February 1973
3. Accession No.
w
5. ReportDate May, 1972
ff.
8. Performing Organization
Report No.
10. Project No.
11. Contract/Grant No.
WPD-93-03;93-04
13. Type of Report and
Period Covered
16, Abstract
Sugarbeet factory transport (flume) water wastes were treated in pilot-sized anaerobic,
facultative and aerobic ponds to remove BOD. Physical, chemical and mechanical data
were collected on the performance of each pond which showed cause for abandoning the
facultative phase of treating. BOD removal in the anaerobic pond was a linear function
of the BOD loading and up to a loading of 2,000 pounds of BOD per acre per day, 80%
removal was accomplished with the assistance of mechanical aeration. The algae
(aerobic), pond was mixed by means of four 12,000 gpm propeller pumps. Some unseparated
algae pond effluent was recycled to the anaerobic pond providing organic nitrogen,
phosphorus and "seed" for the microbial transformations. Additional nutrients were
required for maximum performance. The system was effective in converting soluble
BOD to insoluble BOD. The report contains 42 figures and 11 tables which show
potential commercial application of certain segments of the processes investigated.
17a. Descriptors
17b. Identifiers
Waste Water Treatment, Wastewater Quality Control Pollution Abatement,
Pilot Treatment Facility, Industrial Waste Treatment.
Sugarbeet Waste Treatment, Anaerobic Pond, Facultative Pond, Aerobic Pond,
Algal Growth Nutrient Addition, Odor Control.
17c. COWRR Field & Group
18. Availability
19. Security Class.
(Report)
20'. Security Class.
(Page)
21. No. of
Pages
22. Price
Send To:
WATER RESOURCES SCIENTIFIC INFORMATION CENTER
U.S. DEPARTMENT OF THE INTERIOR
WASHINGTON, D. C. 20240
Abstractor
Institution
WRS1C 102 (REV. JUNE 1971)
«U.S. GOVERNMENT PRINTING OFFICE:1973 514-153/197 1-3
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, North Carolina 2712>
Official Business
Special Fourth-Glass Rate
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