United States
Environmental Protection
Agency
Robert S Kerr Environmental
Laboratory
Ada OK 74820
.r Fp f. -f 00/2-7 '<-.-
J>, iy '978
Research and Development
Land Application
of Wastewater
Under High Altitude
Conditions
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U.S. Environmental
Protection Agency, have been grouped into nine series. These nine broad cate-
gories were established to facilitate further development and application of en-
vironmental technology. Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface in related fields.
The nine series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioeconomic Environmental Studies
6. Scientific and Technical Assessment Reports (STAR)
7. Interagency Energy-Environment Research and Development
8. "Special" Reports
9. Miscellaneous Reports
This report has been assigned to the ENVIRONMENTAL PROTECTION TECH-
NOLOGY series. This series describes research performed to develop and dem-
onstrate instrumentation, equipment, and methodology to repair or prevent en-
vironmental degradation from point and non-point sources of pollution. This work
provides the new or improved technology required for the control and treatment
of pollution sources to meet environmental quality standards.
This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia 22161.
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EPA-600/2-78-139
July 1978
LAND AfTLTeHTreN DF WASTEWATER
UNDER HIGH ALTITUDE CONDITIONS
by
John Borrelli
Robert D. Burman
Ronald H. Delaney
Joseph L. Moyer
Hugh W. Hough
Barren L. Weand
University of Wyoming
Laramie, Wyoming 82071
Grant No. R803571
Project Officer
Lowell E. Leach
Wastewater Management Branch
Robert S. Kerr Environmental Research Laboratory
Ada, Oklahoma 74820
ROBERT S. KERR ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
ADA, OKLAHOMA 74820
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DISCLAIMER
This report has been reviewed by the Robert S. Kerr Environmental
Research Laboratory, U.S. Environmental Protection Agency, and approved
for publication. Approval does not signify that the contents necessarily
reflect the views and policies of the U.S. Environmental Protection
Agency, nor does mention of trade names or commercial products constitute
endorsement or recommendation for use.
ii
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FOREWORD
The Environmental Protection Agency was established to coordinate
administration of the major Federal programs designed to protect the
quality of our environment.
An important part of the agency's effort involves the search for
information about environmental problems, management techniques and new
technologies through which optimum use of the nation's land and water
resources can be assured and the threat pollution poses to the welfare
of the American people can be minimized.
EPA's Office of Research and Development conducts this search
through a nationwide network of research facilities.
As one of these facilities, the Robert S. Kerr Environmental
Research Laboratory is responsible for the management of programs to:
(a) investigate the nature, transport, fate and management of pollutants
in groundwater; (b) develop and demonstrate methods for treating waste-
waters with soil and other natural systems; (c) develop and demonstrate
pollution control technologies for irrigation return flows; (d) develop
and demonstrate pollution control technologies for animal production
wastes; (e) develop and demonstrate technologies to prevent, control or
abate pollution from the petroleum refining and petrochemical industries;
and (f) develop and demonstrate technologies to manage pollution resulting
from combinations of industrial wastewaters or industrial/municipal
wastewaters.
This report contributes to the knowledge essential if the EPA is to
meet the requirements of environmental laws that it establish and enforce
pollution control standards which are reasonable, cost effective and
provide adequate protection for the American public.
William jC. Galegar
Director
Robert S. Kerr Environmental Research Laboratory
iii
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ABSTRACT
The objectives of this study were to monitor and evaluate the nutrient,
crop, and hydrologic parameters affecting the Thayne, Wyoming wastewater
treatment system. Cheeseplant wastewater and municipal sewage were mixed,
pretreated, and applied to a 15 hectare sprayfield on a year-round basis.
An ice pack formed during November or December, depending on weather condi-
tions, and lasted through the middle of April. Samples of groundwater and
water from adjacent springs have shown that after three consecutive years
(1975-77) of spraying wastewater on the field and with a build-up of the ice
pack each winter, no significant amounts of pollutants have reached the
groundwater .
Organic nitrogen was oxidized as it traveled through the ice pack and
upper part of the soil mantle during the winter. Reduction of BOD 5, COD, and
nitrogen forms to migrate in the ice pack was observed, clearly showing the
concentration of these parameters at the surface and bottom of the ice pack.
Garrison creeping foxtail appeared to be most adapted to the sprayfield
of those species tested. Reed canarygrass, smooth brpmegrass, and western
wheatgrass were also able to survive the harsh environment of the sprayfield.
The forages studied could, at specific stages of growth, contain sufficient
a-N to be toxic to livestock.
This report was submitted in fulfillment of Grant No. R803571 by
The University of Wyoming under the sponsorship of the U.S. Environmental
Protection Agency. This report covers the period May 1, 1975, to May 1, 1978,
and work was completed as of January 1, 1978.
iv
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CONTENTS
Foreword
Abstract £y
List of Figures vi,
List of Tables
Acknowledgements
Sections
1. Introduction 1
2. Conclusions 2
3. Recommendations 3
4. Site Description and Experimental Procedures 4
5. Environmental Monitoring 14
6. Agronomic Studies 32
7. Treatment of Wastewater in a Sprayfield Ice Pack .... 44
8. Management and Design Recommendations for Sprayfield . . 57
9. References 63
10. Appendices
I. Results of Water Quality Monitoring 66
II. Results of Clalmatic Monitoring 86
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FIGURES
Number Page
1 Site map for Thayne, Wyoming, wastewater system 5
2 Schematic of Thayne, Wyoming wastewater system 6
3 Location of monitoring sites 7
4 Field location of the three individual agronomy studies 12
5 Barley strips planted in June, 1977 15
6 Ponded condition in sprayfield return channel 16
7 North spring located below sprayfield 18
8 Average soil nitrogen levels for the 30 cm depth 23
9 Soil nitrate concentrations for seven forage species irrigated
with three treatments under controlled environments at the
conclusion of the study. Initial concentration was 12 ppm . . 40
10 Soil phosphorus concentrations for seven forage species irri-
gated with three treatments under controlled environments
at the conclusion of the study. Initial concentration was
17 ppm 41
11 Location of ice pack sampling points 45
12 Sampling of ice pack. 47
13a Location of lysimeters between laterals 48
13b Detail of typical 15 centimeter lysimeter 48
14 Sprayfield covered with ice, April 1977 58
15 Severe build up of ice around sprinkler head 60
16 Ice build up to top of riser 60
17 Solution channel in ice pack 61
18 Melting ice from around riser by removal of sprinkler head ... 62
19 Mean monthly temperatures for Thayne, Wyoming 89
20 Monthly precipitation for Thayne, Wyoming 90
21 Mean wind speed for Thayne, Wyoming 91
vi
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TABLES
Number
1 Composition of Three Irrigation Treatments Used in Controlled
Environment Pot Experiments 12
2 Soil Nitrogen Concentrations for 1975 19
3 Soil Nitrogen Concentrations for 1976 20
4 Soil Nitrogen Concentrations for 1977 21
5 Soil Phosphorus Concentrations in ppm by Form, Depth, and
Sampling Date at the Agronomy Plot Area of the Disposal Site. 25
6 Weight of Soil Phosphorus in Kilograms per Hectare by Form,
Depth, and Sampling Date at the Agronomy Plot Area of the
Disposal Site 26
7 Percentages of Total Phosphorus by Form, Depth, and Sampling
Date on the Agronomy Plot Area of the Disposal Site 27
8 Percentages of Phosphorus by Depth Within Form at Each Sampling
Date on the Agronomy Plot Area of the Disposal Site 28
9 Soil Data for the Study Period (1975-1977) on the Agronomy Plot
Area of the Disposal Site 30
10 Quality Factors of 17-Forage Species from Field Plots 33
11 Chemical Composition of 17 Forage Species from Field Plots ... 34
12 Forage Quality and Yield of Four Forage Species Which Survived
the Field Conditions 36
13 Forage Quality and Yield of Reed Canarygrass from a One-and
Five-Cut Harvest Schedule at the Sprayfield 37
14 Effect of Three Irrigation Treatments and Temperature on the
Growth, In Vitro Dry Matter Digestibility (IVDMD), Protein,
and Phosphorus of Seven Forage Species 39
15 Water Quality Data for Ice Pack at Thayne, Wyoming-1976 .... 49
16 Water Quality Data for I Ice Pack at Thayne, Wyoming-1977 .... 50
17 Nutrient and Biological Data for Fourteen Water Sampling
Points 67
18 Heavy Metal Data for Fourteen Water Sampling Points 83
19 Chemical Analysis for Fourteen Water Sampling Points 84
20 Depth to Water Table in Sprayfield 87
21 Hours per Month of Irrigation for Each Section of Sprayfield . . 88
vii
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ACKNOWLEDGEMENTS
The authors wish to thank Mark Greene, George Bunk, David Zwonitzer,
and Gary Rosenlieb for their help in gathering data and in laboratory analy-
ses. They willingly traveled the long distance to Thayne in the dead of
winter and worked in cold weather at less than desirable tasks.
Special thanks is given to Charles Dana and Carl Ransom for their help
with the work at Thayne. The Town of Thayne has assisted in numerous ways.
Finally, the authors wish to thank Lowell Leach, Project Officer, for
his encouragement and technical assistance.
viii
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SECTION 1
INTRODUCTION
The application of municipal and industrial wastewater to land for
treatment has reached a high state of proficiency in warm climates. It is
only natural that organizations in cold climates would like to use this
technology to solve some of their wastewater problems. As is often the case,
the adaptation of new technology to different environments necessitates
changes in this technology and creates special problems that must be solved
before the systems can perform their intended functions. It was the main
objective of the University of Wyoming to monitor the land treatment system
at Thayne, Wyoming, and to evaluate the nutrient, crop, and hydrologic para-
meters affecting the operation of the system under the severe climatic condi-
tions found at that location.
The Town of Thayne, Wyoming, chose to use a land treatment system for
their wastewater even though the growing season is short and the winter
temperatures can easily reach -40°C. Engineering reports indicated a land
treatment system to be cost effective and would allow the wastewater to be
reclaimed without any direct discharge to surface waters and very little if
any pollutants being discharged to receiving groundwater. In addition, the
system would not take valuable agricultural land out of production.
The system, once in operation did not meet the expectation of the Town
of Thayne for a number of reasons. Most of the dissatisfaction with the
system does not pertain to the objectives of this report and will not be
addressed. This report will address itself to the results of the monitoring
program and to answering the following questions: (1) will land treatment of
combined municipal and industrial wastewater work under high altitude condi-
tions where severe cold weather is normal, and (2) what problems exist in the
land treatment process under these conditions and how should they be handled?
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SECTION 2
CONCLUSIONS
The land treatment system used by Thayne, Wyoming, for treating its
wastewater did work. This was concluded because no significant amounts of
pollutants above background levels, other than total dissolved solids, were
found in the groundwater below the sprayfield. The pollutants examined
encompass both conservative and nonconservative materials and living matter,
thus groundwater pollution from the land treatment system seems remote.
Other conclusions about the wastewater treatment system are as follows:
1. High strength wastewater can be treated by land application on a
year-round basis in very cold climates.
2. The ice pack that results from winter-time application works in
harmony with the soil matrix to treat the wastewater.
3. Formation of an ice pack can be used as a means of liquid storage
during the winter months as an alternative to the use of large
holding lagoons.
4. Garrison creeping foxtail, reed canarygrass, smooth bromegrass, and
western wheatgrass were able to survive the harsh environment of
the sprayfield.
5. The controlled environment study indicated that the low temperatures
at the field site may limit nutrient uptake although this was not
as evident in the field grown forage.
6. When the combination of nutrient uptake, forage yield and quality
of the livestock feed was considered, Garrison creeping foxtail
appeared to be the most adapted to the sprayfield of those species
tested.
7. The forage crop under the field site studied could, at specific
stages of growth, contain sufficient NOa-N to be toxic to livestock.
8. Even during the winter there were significant reductions of BOD5
and COD in the upper 45 cm of the soil mantle although these de-
creases were probably attributable to filtration of the organic
matter by the soil as well as an indication that some biological ,
processes were occurring during the winter.
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SECTION 3
RECOMMENDATIONS
The wastewater treatment system at Thayne operated under very severe
climatic conditions. Since limited management information is available for
land application systems under such conditions, many problems with manage-
ment as well as system design were noted. To improve the operation and
design of similar systems, the following recommendations are made:
1. Forage harvested from system should be analyzed for NO3 as levels
toxic to livestock may occur.
2. Establish the desired perennial forage species prior to or as early
as possible after the initial operation of the system. This will
decrease the buildup of weed species adapted to the harsh environ-
ment.
3. All laterals and mains should be buried a sufficient depth to pre-
vent freezing. Soil should not be piled up over the pipes in lieu
of a deep trench. The piled soil prevents normal farming operations
and the plants that grow in these piles can cause odor and weed
problems.
4. All laterals and mains should drain back to the pump wet well to
prevent any water in risers and sprinkler heads after the stoppage
of spraying.
5. A cleanout valve should be placed at the end of each lateral.
6. Effluent sprayed in the winter should have a temperature of 4°C or
above to prevent any serious buildup of ice on the sprinkler heads.
7. No more than two-thirds of the sprayfield should be used during
the winter. The remaining one-third of the sprayfield should be
saved and used in 'the spring at the time of ablation of the ice
pack. If this procedure is followed, no additional water will be
added to the area under the ice pack and water logging of the soil
at the time of ablation can be minimized.
8. Set times should be 30 minutes or less during the winter months.
Following ablation of the ice pack, the irrigation schedule should
be returned to a summer time mode. During the summer any section
should not be irrigated more than once per week. More frequent
irrigations will keep soil temperatures low and retard plant growth.
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SECTION 4
SITE DESCRIPTION AND EXPERIMENTAL PROCEDURE
LOCATION OF STUDY
The wastewater treatment system at which this study was conducted is
located at Thayne, Wyoming, and is in the center of the Star Valley (see Fig.
1). The winters in Star Valley are considered severe. According to Becker,
et al., (1961), an average of 18 days (from 29 years of recorded temperature
data) separates the last 0°C temperature in the spring and the first 0°C
temperature in the fall at nearby Afton, and an average of 54 days separates
the last -2°C frost in the spring and the first -2°C frost in the fall.
Temperatures of -1°C to 1°C are considered to cause a light freeze. In the
spring a light freeze may kill crops due to their young age.. In the fall a
light freeze will halt the growth of most plants. Temperatures of -4°C to
-2°C result in so-called moderate freeze. A moderate freeze will cause
moderate to heavy damage to plants which would survive a light freeze (e.g.,
fruit trees, lettuce, celery, etc.). Semihardy plants, such as tomatoes,
will be damaged. A severe freeze will occur at temperatures of -6°C to -4°C,
killing the most hardy annuals and driving perennials into dormancy. At
nearby Afton, the average number of days between the last -4°C temperature
in the spring and the first -4°C temperature in the fall is 110 days. This
indicates an average growing season of 110 days for hardy crops such as the
forage crops used and recommended for the land treatment system.
DESCRIPTION OF THE SYSTEM
The wastewater treatment system at Thayne is very simple. With a design
average flow of 1325 m3/day and a design peak flow of 4136 m3/day, the waste-
water enters a lined aerated lagoon which has a capacity of 1332 m3 (see Fig.
2). Over 90 percent of the wastewater flow arises in the cheese factory
with the remainder being domestic wastewater from the town of Thayne. At
design average flow, the hydraulic detention time in the aerated lagoon will
be approximately 24 hours. The influent flow is variable and has ranged from
632 to 1541 m3/day. From the aerated lagoon the wastewater flows into a
storage lagoon with a capacity of• 4700 m . The wastewater is pumped from the
bottom of the storage lagoon and sprayed on a 15 hectare sprayfield. There
is no return of settled solids from the storage lagoon to the aerated lagoon,
i.e., there is no cell recycle. Application of wastewater is rotated to
different sections of the sprayfield each day six days a week via a high
pressure solid set spray irrigation system, with each of the six sections
of the sprayfield being sprayed once per week. Only small amounts of waste-
water are generated on Sundays. Treated wastewater can leave the system
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WYOMING
I
ID. ! WY
Land Applicatic n
Figure 1. Site map for Thayne, Wyoming, wastewater system.
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Interceptor
Line
Comminutor
Aerated Lagoon
Chlorinator
Sprinkler
Pump
V V V v v ^ v
To Spray Field
Storage
Pump ^
Collector for any
Surface Runoff
Figure 2. Schematic of Thayne, Wyoming, wastewater system.
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only by deep percolation and/or evapotranspiration. All surface runoff from
the sprayfield is collected in a channel on the downslope sprayfield side of
a dike, and the only exit from the channel is back to the storage lagoon
from where the wastewater will be resprayed on the sprayfield. The system
was designed to prevent surface discharge to adjacent water courses, mainly
Flat Creek. Operation of the system first began in January of 1975.
PROCEDURE FOR ENVIRONMENTAL MONITORING
The environmental monitoring consisted of (1) water sampling that at-
tempted to ascertain the quality and changes in the wastewater from the time
the water arrived at the plant until it reached the groundwater, (2) obser-
vation of climatic variables, and (3) soil sampling. Additional information
was obtained on water quality during the investigation of the ice pack.
This information is presented in Section 7.
Water Quality Monitoring
Shown in Figure 3 are the location of the 14 monitoring sites. They
consist of the influent, water leaving the aerated lagoon, water leaving the
holding lagoon, groundwater at 7 wells, water from 2 springs located below
the spray field, water from an underdrain located below the lagoons, and
water from Flat Creek at a site immediately below the sprayfield.
Samples were analyzed for nitrate (NOa), nitrite (NOa), ammonia
total Kjeldahl nitrogen (TKN) , total organic carbon (TOG), five-day biologi-
cal oxygen demand (BODs), chemical oxygen demand (COD), total suspended
solids (TSS), phosphate (PO^) , pH, specific conductance, and fecal coliforms.
All samples were analyzed according to "Standard Methodsfi (1971) after being
preserved in the field and in transport according to Environmental Protection
Agency recommendations for sample preservations (EPA, 1971) . Spot sampling
for heavy metals and certain inorganic constituents was also done. All the
results are presented in Appendix I.
Climatic Monitoring
Regular monitoring of the climate began during the summer of 1975. Re-
cords were kept on air temperature, relative humidity, soil temperatures at
different depths within the \sprayf ield, pan evaporation, wind, and precipi-
tation. Solar radiation was collected during the latter part of the study
period.
Missing data, where possible, were replaced with data from Bedford,
Wyoming, which is located only 4 miles from Thayne. The results from the
climatic monitoring are presented in Appendix II.
Soil Monitoring
Soil samples were from 30, 60, 90, and 120 cm depths in the sprayfield.
Most of the soil samples were taken next to the agronomy plots (see Fig. 3)
although some tests were taken at the north end of the field. Most of the
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Flat Creek
oo
Spring
Return Channel
North Spring
o
H
w
f^
s
SLOPE TO DRAIN
-0-
1 Aerated Lagoon
2 Storage Lagoon
3 Lysimeter Location
4 Ice Pack Sampling Area
5 Agronomy Plots
Wells
-Dike
SLOPE TO DRAIN
t
I
o
H
s
C/3
Figure 3. Location of monitoring sites.
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tests taken were for the purposes of determining changes in nutrient levels.
Two sets of samples taken on May 26, 1976 and August 27, 1976 were assayed
for heavy metals and to determine if any change in heavy metals were occur-
ring. Results are presented in Section 5.
FORAGE ASSESSMENT
The following forage species were irrigated with wastewater from the
Thayne system: 'Rise1 Reed canarygrass (Phalaris arundinacea L.), 'Manchar'
smooth bromegrass (Bromus inermis Leyss.)> 'Regar' meadow bromegrass (Bromus
biebersteinii Roem, and Schult.), 'Kenmont' tall fescue (Festuca arundinacea
Schreb.)> 'Garrison' creeping foxtail (Alopecurus arundinaceus Poir.),
'Dawson' alfalfa (Medicago sativa L.), and 'Eski' sainfoin (Onobrychis
viciaefolia Scop.)- Tw° controlled environment pot experiments and field
plots at Thayne, Wyoming, were used to evaluate the seven forage species
for growth and quality.
Selection of Test Species
The grass and legume species used in this study were recommended for
similar areas of climatic conditions and altitude in Wyoming. 'Regar' mea-
dow bromegrass and 'Manchar' smooth bromegrass are cool season grasses that
are moderate sod forming plants. They both have early spring growth and will
remain green until late fall (Kail et al., 1972, Seamands and Kolp, 1975).
Both are drought-hardy but 'Regar' will not tolerate poorly drained soils or
high irrigation rates.
'Kenmont' tall fescue and 'Rise' reed canarygrass are both cool season
grasses but are adapted to a wide variety of conditions. They are both
tolerant of poorly drained soils and high irrigation rates (Kail et al.,
1972, and Moyer and Seamands, 1975). They are both sod-formers, which may
be beneficial in erosion control under high irrigation rates. Both have the
disadvantage of having poor palatability and are not well accepted by
livestock.
'Garrison' creeping foxtail is also a cool-season sod-forming grass.
It produces well under irrigated conditions and can tolerate wet marshy areas
(Kail et al., 1972). It has early spring growth but has poor seedling vigor,
thus it is slow to establish. \
The two legume species, 'Dawson' alfalfa and 'Eski1 sainfoin, were
chosen for their adaptability to a short season and cool climate. 'Dawson1
is a wilt resistant, winter hardy variety that has done well under irrigated
yield trials in Wyoming (Richardson and Roehrkasse, 1974). 'Eski1 sainfoin
has the distinct advantage of being resistant to the alfalfa weevil and does
not cause bloat. 'Eski1 has slow regrowth but has had favorable yields in
Montana under irrigation (Krall et al., 1971). It has the disadvantage of
poor stand persistance on some sites.
Ten additional species adapted to a short growing season were esta-
blished in the sprayfield. The ten species which were planted in two
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replications were as follows: 'Chinook1 orchardgrass (Dactylis glomerata),
'P-15594' creeping wildrye (Elymus triticoides), 'P15590' basin wildrye
(Elymus cinereus), 'Critana' thickspike wheatgrass, (Agropyron dasystachyum),
'Rosanna' western wheatgrass (Agropyron smithii), 'Sodar' streambank wheat-
grass (Agropyron riparium), 'Bromar' mountain bromegrass (Bromus marginatus),
'Drummond' timothy (Phleum pratense), 'Park' Kentucky bluegrass (Poa praten-
sis), and 'Lutana1 cicer milkvetch (Astragalus cicer).
Field Study
The seven forage species were established in the sprayfield in June
1975. Plots were 1.83 by 4.57m with four replications of each species (see
Fig. 4). Under normal operation of the wastewater system, the plots would
receive an irrigation of wastewater once a week. The forage species were
evaluated for yield and quality as well as nutrient removal and accumulation
potential.
Reed canarygrass plots were established to study the effect of harvest
schedules on forage yield and quality (see Fig. 4).
Ten additional species were also established adjacent to the field plots.
They were sampled and analyzed for quality and chemical composition using
the same methods as used for the seven primary species.
Controlled Environment Study
Soil from the sprayfield at Thayne, Wyoming, was collected, air-dried
and sieved through a 1 cm screen to remove large rocks. Two kgs of the soil
(Greyback gravelly loam; Typic cryoboroll) were placed in each of one-hundred-
twenty-six 15.5 by 13.5 cm plastic pots and planted with one of the seven
forage species. Plants were thinned to three seedlings per pot, placed in
a greenhouse at a temperature of 21°C and watered with distilled water.
After the plants were established and reached a uniform height, they were
cut at 2.5 cm above the soil surface and the study was begun.
The seven species were placed in a growth chamber (Conviron PGW 36) with
a 20/10°C day-night temperature regime, 16-hour day length, 50% relative
humidity and 48.4 klux light intensity at the plant canopy. The night tem-
perature was reduced from 20 to 10°C over a 6-hour period, held at 10°C for
2 hours, then increased to 20°C over a 4-hour period to simulate conditions
at the Thayne irrigation site.
Three irrigation treatments with six replications were used as follows:
1. Effluent - the effluent was collected at the site from a sprinkler
head and stored at 5°C. Effluent characteristics and nutrient
levels are in Table 1. The effluent-treated pots were watered daily
with 90 ml of effluents which coincided with the average 6.22 cm/
week on the field disposal site.
2. Synthetic Effluent - the synthetic effluent consisted of the same
concentrations of inorganic nitrogen, phosphorus, and potassium as
10
-------
1 N
V 1
\
1
\
/
\
i
l
\
/
\
/
\
i* ,
11.9 m
10
Species
Study
12.2 m
**
12.8 m
7
Species
Study
I
9.1 m
\
9.1 m
)
18.3 m
\
/
f
\
f
\
V
c
P
<]
<1
CS
f \
m^fm
\
X
* Sprinkler Head
** Reed Canarygrass
Harvest Schedule Study
24.4 m
Figure, 4. Field location of the three individual agronomy studies.
11
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TABLE 1. COMPOSITION OF THREE IRRIGATION TREATMENTS USED IN
CONTROLLED ENVIRONMENT POT EXPERIMENTS
N (inorganic)
N (Kjeldahl)
P
K
so=
s
Ca
Na
Cl
F
Mg
TDS
Effluent Control
0.1 10.1
31.0
0.3 6.5
61.0 33.3
32.0
45.0
100.0
58.0
67.0
1.6
26.0
900
IT/IT
pll
5.1 6.0
Synthetic
Effluent
0.1
0.3
61.0
5.1
12
-------
the effluent (Table 1). The sources of these elements were:
NHitN03 for N, HsPOit for P, and KOH for K. The pH was adjusted to
5.1 with HC1. Pots treated with the synthetic effluent were also
watered with 90 ml per day.
3. Control - the control treatment concentrations were based on recom-
mended fertilizer applications according to soil tests (Table 1).
The control pots were given 90 ml of the control solution once
weekly, and 90 ml of distilled water on the other days.
The pots' locations were randomized in the growth chamber and rerandom-
ized each week throughout the experiment. Harvest occurred after 57 days of
growth.
The experiment was continued in a greenhouse under conditions of 23/18°C
day-night temperature, 16-hour day length and 60% relative humidity. Water-
ing continued with the three treatments as before, and the plants were
harvested after 34 days. To determine the effect of irrigation treatment on
soil nutrient levels, soil samples from a composite of three replications
were analyzed for nitrate and phosphorus by the Agricultural Consultants
Laboratory, Brighton, Colorado.
The harvested plant samples were dried in a convection drying oven at
60°C for 6 days and weighed for dry forage yield before being ground to a
fineness of 0.05 cm. Percentage protein was determined from 30 mg samples
by the micro-Kjeldahl steam-distillation method (Association of Official
Agricultural Chemists, 1955). In vitro dry matter digestibility (IVDMD)
(Georing and VanSoest, 1970) was assayed using 500 mg of tissue. Rumen
fluid for the IVDMD tests was obtained from a steer on a mixed grass-alfalfa
diet. Phosphorus was determined by ashing a 500 mg sample at 200°C, 400°C,
and 600°C for 2 hours at each temperature, extracting with .01N HC1 and
assaying by the Elon colorimetric method (Fiske and Subbarow, 1925).
13
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SECTION 5
ENVIRONMENTAL MONITORING
INTRODUCTION
One of the main purposes of the environmental monitoring study was to
assess the system's ability to treat Thayne's wastewater. The evaluation of
the monitoring results should be tempered with the fact that the treatment
system was never fully completed although the system has operated for three
years. It is the opinion of the authors, however, that the system was ade-
quate to make some judgement on the ability of this type of system to
renovate wastewater.
STATUS OF SYSTEM
The system was built as described in Section 4 except for the return
channel on the southwestern portion of the field. This return channel was
not needed except during the summer of 1977 after part of the field was
planted to barley (see Fig. 5). The planting operation destroyed the grass
and the barley died. Without actively growing vegetation the field's infil-
tration rate decreased to the point that surface runoff occurred after ap-
proximately one-hour of irrigation (0.9 cm of water). Runoff was kept to
a minimum by the operational "procedures of the system's operator.
Another factor that could affect the wastewater treatment was the over-
loading of certain portions of the field due to pipeline failure. The most
serious problem occurred during the winter of 1975-76 when the mainline
serving the southern two-thirds of the field broke. The northern one-third
of the field received all the wastewater from about the first of January,
1976 until the middle of May, 1976. There were numerous other small problems
with the system but they would be classified as minor by comparison or did
not significantly affect the operation of the system.
RESULTS OF WATER QUALITY MONITORING
Presented in Appendix I are the data collected from the 14 water moni-
toring sites. The strength of the influent, using COD as a measure, entering
the Thayne treatment system averaged 13,200 mg/1 (based on point samples).
This is extremely strong when one considers that strong domestic sewage
would have a value for COD around 1000 mg/1 (Metcalf & Eddy, 1972). The
effluent that was applied to the sprayfield averaged 9,700 mg/1 (based on
point samples). Thus, it appears that the pretreatment removed approximately
14
-------
Figure 5. Barley strips planted in June, 1977.
25 percent of the organic load. It is of interest to note that the waste-
water leaving the aerated lagoon averaged only 5,700 mg/1 (based on point
samples). This would suggest the holding lagoon was manufacturing COD.
Surprisingly enough, data from the Wyoming Department of Environmental Qual-
ity suggests identical conclusions. The amount of algae put into the holding
lagoon by the sprayfield return channel (see Fig. 6) is an unknown factor and
could possibly explain the increase in COD in the holding lagoon. Records
were not kept on the volume of water returning to the holding lagoon and it
was judged to be a minor amount. The ponding of the water in the return
channel was one of the minor problems experienced by the Thayne system.
i
After almost 3 years of continuous operation the overall renovation
of the wastewater appears to be excellent. The groundwater beneath the
field that receives the treated wastewater has not been affected. An exam-
ination of groundwater data indicated that the pollution parameters BODs,
.nitrate, ammonia, COD, phosphate, and fecal coliforms were either absent or
were approximately at the same concentrations for the groundwater receiving
renovated wastewater as in the groundwater unaffected by the wastewater. The
downstream wells (wells 1, 2, 3, and 4) and the springs should receive the
renovated water, while the upstream wells (wells 5, 6, and 7) should be free
of any wastewater. It should be noted that the groundwater samples from the
wells were taken from the top of the aquifer and were not homogeneous water
samples from the aquifer.
15
-------
•
Figure 6. Ponded condition in sprayfield return channel.
The treatment of the wastewater in the sprayfield does cause some deter-
ioration of the groundwater. Although the organic and biological pollutants
were removed, there was an increase in total dissolved solids (IDS). The
average TDS during the monitoring period was 176 mg/1 for the water in the
upstream wells and 472 mg/1 for the downstream wells. During May of 1977,
immediately following ablation of the ice pack, the water in the upstream
wells had an average TDS of 294 mg/1 while water in the downstream wells had
an average TDS of 871 mg/1. The effluent averaged 571 mg/1 of TDS during the
monitoring period.
The increase in TDS would be expected for two reasons. First, the efflu-
ent being applied to the field had a higher average TDS than did the incoming
groundwater as indicated by the upstream wells. Second, anytime one passes
water through a soil column some additional salts are dissolved. The soil in
the sprayfield has a definite calcareous layer 45 to 60 cm below the surface.
A significant increase in TDS most likely occurs for water passing through
this soil.
I
Increases in TDS of the groundwater were kept relatively low because of
the apparent high rate of groundwater movement below the field. The high
rate of groundwater movement is evidenced by 1) the rate that water percolated
into the lagoons during construction, 2) the rapid increase and decrease in
the water table below the field, and 3) the many large springs that are
16
-------
located below the sprayfield and along the full course of Flat Creek that
have flow rates greater than 25 liters per second (see Fig. 7).
High COD and low BOD5 values observed in Flat Creek and the north and
south spring samples during June and July of 1975 and 1976 could be attri-
buted to the following factors: 1) toxicity to bacteria in the waters that
caused low BOD5 readings, or 2) cellulose or similar substances that are
slowly biodegradable and hence produce low BOD5. The cellulose-like sub-
stance could have been washed into the waters by the spring runoff.
The high COD values in the water from the observation wells during the
same period are more difficult to explain. One possible explanation could
be the presence of reduced inorganic substances such as ferrous iron sulfide,
or ammonia (note presence of ammonia in wells 2 and 4). The important fact,
however, is that the increase cannot be directly attributable to the spray-
field since the increased COD also occured in water not coming from the
sprayfield.
RESULTS OF CLIMATIC MONITORING
To evaluate the climatic conditions at Thayne during the monitoring
period with long-term climatic conditions, a comparison was made with the
climatic records of Afton, Wyoming. Afton is located in the same mountain
valley as Thayne (see Fig. 3) and has approximately the same climate. The
elevation at the Afton weather station is 1,864 meters while the elevation of
the sprayfield is approximately 1,814 meters. Since elevation is the princi-
pal cause for climatic differences within the Star Valley, the climatic con-
ditions at Thayne and Afton should be approximately the same given only a 50
meter elevation difference.
Data from the climatic monitorings are presented in Appendix II. Com-
paring the temperatures and rainfall for late fall for 1975 and 1976, the
1975 fall was relatively wet and cold while the 1976 fall was relatively
warm and dry. This was a major contributing factor for having the ground
remain unfrozen during the winter of 1975-76 and frozen during the winter of
1976-77. It will be shown in Section 7 that it is preferable to have the
ground remain unfrozen. The relatively cold winter of 1976 and the relative-
ly warm winter of 1977 apparently affected the density of the ice pack (see
Section 7).
Shown in Fig. 21 are the average monthly wind speeds. For the high
pressure sprinkler system used, the wind during many hours of the month were
high enough to significantly lower the uniformity of application. It should
be noted that a characteristic pattern of wind occurrence in the valley is low
winds during the morning hours and increasing winds in the afternoon hours.
This would force curtailment of sprinkling many afternoons if there was an
operational criterion for maximizing the uniformity of application.
Soil temperatures were taken inside the sprayfield and adjacent to it.
At the 2.5 cm depth the soil temperature outside the sprayfield was as much
as 10°C greater than inside the field. This means the time between
17
-------
Figure 7. North spring located below sprayfield.
irrigations should be as long as possible in order to allow the soil temper-
ature to rise and promote plant growth and microbial activity.
SOIL NITROGEN
Soil nitrogen data for 1975, 1976, and 1977 are presented in Tables 2,
3, and 4. The soil samples were taken adjacent to the agronomy plots (see
Fig. 3), and a year-end sampling from within the Reed canarygrass date-of-
cutting plots. Samples were taken every 30 cm down to the 120 cm depth.
Adjacent to the plots, the vegetation was initially a bromegrass-alfalfa
mixture but during the experiment the alfalfa was replaced by an invasion of
bluegrass.
Soil nitrogen concentration generally declined in the upper 30 cm during
1977. However, an increase was noted in the July 31 sampling, returning to
May levels as a result of increased effluent nitrogen content. The 60 cm
and 120 cm levels exhibited no net change in reduced N during 1977, but the
90 cm level doubled in concentration. Since the other N fractions showed no
such change, organic nitrogen must have leached to the 90 cm depth because
of the higher rates applied and/or been converted from other N forms by
plants or microorganisms. Under the Reed canarygrass, N concentrations were
generally higher than adjacent to the plot area, except at the 90 cm level.
18
-------
TABLE 2. SOIL NITROGEN CONCENTRATIONS FOR 1975
Sample Date
Adjacent to Plots June 4
30 cm depth
60 " "
90 " depth
120 " depth
NO 3 -N
(ppm)
9
3
3
<2
Nnt-N
(ppm)
26
26
20
7.5
Total N
(Reduced, %)
0.36
0.22
0.18
0.07
Adjacent to Plots
15 cm depth
Adjacent to Plots
30 cm depth
60 " "
90 "
120 " "
June 27
Adjacent to Plots August 1
15 cm depth
September 17
26
39
140
48
0.33
0.39
5
10
9
5
52
44
25
6
0.28
0.16
0.06
0.03
19
-------
TABLE 3. SOIL NITROGEN CONCENTRATIONS FOR 1976
Sample
Adjacent to Plots
30 cm depth
60 " "
90 " "
120 " "
North side
30 cm depth
60 " "
90 " "
120 " "
Adjacent to Plots
30 cm depth
North side
30 cm depth
Adjacent to Plots
30 cm depth
60 " "
90 " "
120 " "
North side
30 cm depth
Date NO^-N
(ppm)
May 26
19
12
7
6
May 26
24
14
6
5
July 28
14
July 28
54
August 27
25
18
10
10
August 27
22
Nflt-N
(ppm)
44
32
18
15
90
36
31
11
30
68
104
52
21
22
51
Total N
(Reduced, %)
0.31
0.20
0.12
0.08
0.48
0.22
0.12
0.13
0.30
0.40
0.38
0.23
0.13
0.08
0.34
20
-------
TABLE 4. SOIL NITROGEN CONCENTRATIONS FOR 1977
Sample Date
Adjacent to Plots May 12
30 cm depth
60 " "
90 "
120 " "
N07-N
(ppm)
10
8
•3
2
(ppm)
129
105
42
7
Total N
(Reduced, %)
0.43
0.22
0.07
0.04
30 cm depth
30 cm depth
30 cm depth
30 cm depth
60 " "
90 " "
120 " "
Under Reed Canarygrass
30 cm depth
60 " "
90 "
120 " "
June 8
July 7
July 31
September 13
September 13
49
30
134
175
51
91
0.36
0.34
0.43
7
5
4
2
5
7
6
3
61
25
17
4
49
27
21
13
0.23
0.21
0.18
0.05
0.28
0.30
0.12
0.10
21
-------
Over the entire study period, total N seems to have returned to
levels similar to those under the previous cropping system. The higher N
application rates of 1976 (northside) and 1977 were accommodated, but new
equilibrium levels were probably not yet attained. The variations with
depth between the springs of 1975 and 1977 were probably mostly a function
of different crop species as seen earlier between sites in the fall of
1977.
Ammonium concentrations in the soil also generally declined during
1977. There was considerable variation in the top 30 cm because of fluctua-
tions in effluent concentrations of ammonia and total N. The decline in
concentration also occurred deeper in the soil, and changes were moderated
with depth; that is, relative reductions were greater in the 60 cm level
than in the 90 cm level, which were greater than in the 120 cm level.
Since the 90 cm level did not increase in ammonium, leaching alone must
not have been responsible for the organic N buildup at that depth. The
soil under Reed canarygrass was lower in ammonium in the top 30 cm, similar
in the second 30 cm, and progressively higher in the 90 and 120 levels
than the plot samples. Ammonium thus appeared to be moved to greater soil
depths under the Reed canarygrass sod than in the rather open soil of the
area adjacent to the plots.
For the study period ammonium concentrations fluctuated considerably
in the top 30 cm. The variations were due to interaction between seasonal
effects and application schedule. In the top 30 cm, an expected seasonal
pattern might be low initial amounts, increases as ammonification of
organic N proceeded, then reduction as plants and microorganisms used and
"tied up" ammonium. Concentrations at the end of 1976 and beginning the
1977 growing season increased because of heavier effluent applications to
that area beginning in August of 1976. The variation in effluent concen-
trations of N in the summmer of 1977 influenced ammonium concentrations
more than total N. The deeper soil layers were less affected by ammonium
concentration than the top 30 cm; however, data show that ammonia concen-
trations fluctuated considerably.
Nitrate concentrations varied considerably more in the summer of 1977
than at any previous time. The late summer sampling (top 30 cm) produced
the only reading in excess of 60 ppm, and it was over twice the previous
high. Nitrification of the high N effluent had apparently occurred by
that time. However, the nitrate must have been quickly taken up by plants,
denitrified, or leached by the end of the growing season because concen-
trations in the top 120 cm of soil by then had returned to their previous
low levels. Reed canarygrass sod affected concentrations of the soil
slightly, reducing levels in the top 30 cm and increasing levels in the 60
and 90 cm depths.
During the study period, nitrate concentration peaked in late summer,
except when effluent application was deferred until then. Amounts in the
soil were usually within safe limits until nitrogen rich effluent was
applied in the summer of 1977. Even then, apparent leaching was minimal,
but potentially toxic levels of nitrate were accumulated in the forage.
22
-------
LO
ppm
ppm
100
50
120
60
0.4
0.2
Plots
North Side
Reed Canarygrass
NITRATE
e I
AMMONIUM
TOTAL RED N
I // I
7-75 9-75 6-76 8-76
Figure 8. Average soil nitrogen levels for the 30 r.m depth.
6-77
8-77
-------
SOIL PHOSPHORUS
Soil phosphorus data for 1975, 1976, and 1977 are presented in
Tables 5, 6, 7, and 8. Soil samples for these determinations were taken
every 30 cm to the 120 cm depth adjacent to the agronomy plots at the
beginning and ending of each growing season.
The soil phosphorus concentrations of organic, inorganic, and total
phosphorus generally decrease with depth in the soil (Table 5). With
essentially no effluent applications to the agronomy plot area during
the period covered by the first three sample dates, the organic phosphorus
concentrations at all soil depths continually decreased while the total
phosphorus concentration did not change. The inorganic phosphorus
concentration in the first 30 cm did increase in the May 26, 1976,
sample over the two preceding samplings.
Effluent applications on the agronomy plot area started in June of
1976. The August 27, 1976, sampling produced the highest phosphorus
concentrations at all depths and all forms except for organic phosphorus
at the 60-90, and 90-120 cm depths. The spring sampling for 1977 showed
an almost equal decline in amount of organic and inorganic phosphorus
while the 1977 fall sampling showed a recovery of organic phosphorus in
the 0-30 and 30-60 cm depths, while the inorganic phosphorus concentration
declined at the 0-30 cm depth.
The conversion of phosphorus concentration data to quantities
present at the various soil depths was influenced by the amount of soil
present with the rocks and coarse gravels at the different depths. It
was found that 50% of surface 30 cm of depth was soil, and the soil
present was 40, 30, and 20% for the succeeding 30 cm increments of
depth. This meant that the 3000 cubic meter volume for a 30 cm layer
over a hectare was really occupied by 1500, 1200, 900, and 600 cubic
meters of soil at the respective depths. The soils in this area of
Wyoming are not inherently phosphorus deficient. Using the phosphorus
shown in Table 5, the quantities of soil present at each depth were used
to calculate the amounts of each kind of phosphorus present in kilograms
per hectare. The results are shown in Table 6. The decrease in amounts
of all phosphorus forms with increasing depth is very distinct. A
decline of organic phosphorus at all depths for the first three sample
periods was followed by a big increase in the August 27, 1976, sampling
followed by another overwinter decline, then another increase in the
September 13, 1977, sampling. The changes in amounts are larger in the
0-60 cm layers than in the 60-120 cm layers for all forms of phosphorus.
The inorganic phosphorus in the last sample has returned to the level of
the first sample for the 60-120 cm depths but the 0-60 cm depth is
enriched by 35 percent. The organic phosphorus has increased in the top
0-60 cm by 18 percent and decreased in the 60-120 cm depth by 64 percent.
24
-------
TABLE 5. SOIL PHOSPHORUS CONCENTRATIONS IN PPM BY FORM, DEPTH, AND
SAMPLING DATE AT THE AGRONOMY PLOT AREA OF THE DISPOSAL SITE
Depth
cms
6-4-75
9-17-75
Sampling date
5-26-76 8-27-76
5-12-77
9-13-77
Organic phosphorus
0-30
30-60
60-90
90-120
Total
390
405
338
180
1313
262
225
120
90
697
99
83
57
46
285
637
652
243
121
1653
114
311
76
23
524
500
432
91
114
1137
Inorganic phosphorus
0-30
30-60
60-90
90-120
Total
0-30
30-60
60-90
90-120
Total
1485
1395
1462
1170
5512
1875
1800
1800
1350
6825
1688
1350
1080
1260
5378
1950
1575
1200
1350
6075
2138
1434
1422
1319
6313
Total
2237
1517
1479
i 1365
6598
2320
2230
1956
1774
8280
phosphorus
2957
2882
2199
1895
9933
2275
1752
1592
1797
7416
2389
2063
1668
1820
7940
2116
1729
1502
1024
6371
2616
2161
1593
1138
7508
25
-------
TABLE 6. WEIGHT OF SOIL PHOSPHORUS IN KILOGRAMS PER HECTARE BY FORM, DEPTH,
AND SAMPLING DATE AT THE AGRONOMY PLOT AREA OF THE DISPOSAL SITE
Depth
cms
6-4-75
9-17-75
Sampling date
5-26-76 8-27-76
5-12-77
9-13-77
Organic phosphorus
0-30
30-60
60-90
90-120
Total
0-30
30-60
60-90
90-120
Total
585.0
486.0
304.2
108.0
1483.2
2227.5
1674.0
1315.8
702.0
5919.3
393.0
270.0
108.0
54.0
825.0
2532.0
1620.0
972.0
756.0
5880.0
148.5
99.6
51.3
27.6
327.0
Inorganic
3207.0
1720.8
1279.8
791.4
6999.0
955.5
782.4
218.7
72.6
2029.2
phosphorus
3480.0
2676.0
1760.4
1064.4
8980.8
171.0
373.2
68.4
13.8
626.4
3412.5
2102.4
1432.8
1078.2
8025.9
750.0
518.4
81.9
68.4
1418.7
3174.0
2074.8
1351.8
614.4
7215.0
Total phosphorus
0-30
30-60
60-90
90-120
Total
2812.5
2160.0
1620.0
810.0
7402.5
2925.0
1890.0
1080.0
810.0
6705.0
3355.5
1820.4
1331.1
819.0
7326.0
4435.5
3458.4
1979.1
1137.0
11010.0
3583.5
2475.6
1501.2
1092.0
8652.3
3924.0
2593.2
1433.7
682.8
8633.7
26
-------
TABLE 7. PERCENTAGES OF TOTAL PHOSPHORUS BY FORM, DEPTH, AND SAMPLING
DATE ON THE AGRONOMY PLOT AREA OF THE DISPOSAL SITE
Depth
cms
6-4-75
9-17-75
Sampling date
5-26-76 8-27-76
5-12-77
9-13-77
Organic phosphorus
0-30
30-60
60-90
90-120
Total
7.9
6.6
4.1
1.5
20.0
5.9
4.0
1.6
0.8
12.3
2.0
1.4
0.7
0.4
4.5
8.7
7.1
2.0
0.7
18.4
2.0
4.3
0.8
0.2
7.2
8.7
6.0
0.9
0.8
16.4
Inorganic phosphorus
0-30
30-60
60-90
90-120
Total
0-30
30-60
60-90
90-120
Total
30.1
22.6
17.8
9.5
80.0
38.0
29.2
21.9
10.9
100.0
37.8
24.2
14.5
11.3
87.7
43.6
28.2
16.1
12.1
100.0
43.8
23.5
17.5
10.8
95.5
Total
45.8
24.8
18.2
11.2
100.0
31.6
24.3
16.0
9.7
81.6
phosphorus
40.3
31.4
18.0
10.3
100.0
39.4
24.3
16.6
12.5
92.8
41.3
28.6
17.4
12.6
99.9
36.8
24.0
15.7
7.1
83.6
45.4
30.0
16.6
7.9
99.9
27
-------
TABLE 8. PERCENTAGES OF PHOSPHORUS BY DEPTH WITHIN FORM AT EACH SAMPLING
DATE ON THE AGRONOMY PLOT AREA OF THE DISPOSAL SITE
Depth
cms
6-4-75
9-17-75
Sampling date
5-26-76 8-27-76
5-12-77
9-13-77
Organic phosphorus
0-30
30-60
60-90
90-120
Total
0-30
30-60
60-90
90-120
Total
39.4
32.8
20.5
7.3
100.0
37.6
28.3
22.2
11.9
100.0
47.6
32.7
13.1
6.5
99.9
43.1
27.6
16.5
12.9
100.1
45.4
30.5
15.7
8.4
100.0
Inorganic
45.8
24.6
18.3
11.3
100.0
47.1
38.6
10.8
3.6
100.0
phosphorus
38.7
29.8
19.6
11.9
100.0
27.3
59.6
10.9
2.2
100.0
42.5
26.2
17.9
13.4
100.0
52.9
36.5
5.8
4.8
100.0
44.0
28.8
18.7
8.5
100.0
28
-------
The sum of the total phosphorus quantities in the profile for a given
sample date was used as the base for a percentage determination for each form
of phosphorus at each depth. These percentages are recorded in Table 7.
These values confirm the organic phosphorus declines indicated in the pre-
vious table for the September 17, 1975 and the May 26, 1976 samplings. Also
the recovery, loss, and recovery of the organic phosphorus concentrations
of the 0-30 and 30-60 cm depths in the last three samplings are easily seen.
These two horizons have now returned to the relative organic phosphorus pro-
portions found at the start of the experiment. The proportions of inorganic
phosphorus in the soil by depth were 36.6 + 6.9% for 0-30 cm, 23.8+0.9%
for 30-60 cm, 16.4+1.7% for 60-90 cm, and 10.2 + 2.7% for 90-120 cm. The
same kind of a distribution for total phosphorus was 42.4 + 3.9% for 0-30 cm,
28.7 + 3.3% for 30-60 cm, 18.0 + 2.9% for 60-90 cm, and 10.8 + 2.3% for 90-
120 cm.
One further comparison was made to better visualize the proportional
distribution of organic or inorganic phosphorus throughout the profile (Table
8). The sum of the organic phosphorus concentrations for the profile of a
given sampling date was divided into the organic phosphorus concentration
for each depth to give the percentage of the total profile organic phosphorus
that can be found in each respective soil depth. The top two horizons seemed
to alternately be the highest in proportion of the organic phosphorus
present. The third and fourth depths were more consistent, but tended to
decrease from the proportion present at the beginning of the study. The
inorganic phosphorus was more consistently decreasing in proportion present
as the depth increased with 42.0 + 4.1% for 0-30 cm, 27.6+2.6% for 30-60
cm, 18.9+2.8% for 60-90 cm, and 11.7 + 2.5% for 90-120 cm.
Both the organic and inorganic phosphorus concentrations could be signi-
ficantly increased on a short term basis by effluent applications. The
applied organic phosphorus seldom penetrated more than 60 cm into the soil
and was rapidly mineralized so that little or no buildup occurred under nor-
mal cropping practice. The inorganic phosphorus levels held to a consistent
distribution that decreased with depth in the profile.
Other soil characteristics were monitored during the study period, and
the more pertinent data are listed in Table 9. Soil pH was reduced slightly
in the upper foot, because of minor leaching losses of Ca, mg, and other
basic cations. (
Total salts and sodium (Na) each increased during the study period. In
the top 30 cm both were increased more than two-fold, but were still below
thresholds which affect crop growth. Total salts below 4.0 mmhos/cm have no
effect on sensitive plants, and soil with a sodium adsorption ratio (SAR =
Na/CEC) below 0.15 is not considered alkali. The 30-60 cm soil layer in-
creased in salt and Na content, but the increase was less than in the top 30
cm. Greater depths showed no change in Na, but the 60-90 cm depth had an
accumulation of other salts.
Available P and K exhibited increases down to the 90 cm depth. Changes
in available P were similar to those for total P discussed earlier. The
29
-------
TABLE 9. SOIL DATA FOR THE STUDY PERIOD (1975-1977) ON THE
AGRONOMY PLOT AREA OF THE DISPOSAL SITE
Date
6/8/75
5/26/76
8/17/76
5/12/77
9/13/77
Sample
Depth
cm
30
30
60
90
120
30
60
90
120
30
60
90
120
30
60
90
120
pH CEC
meq/lOOg
8.3
8.2
8.5
8.6
8.8
8.2
8.4
8.7
8.8
8.1
8.2
8.5
8.8
8.0
8.2
8.4
8.8
24
22
16
13
12
19
17
13
12
23
22
13
10
23
21
16
9
Salt
mmho.s/cm
0.5
0.6
0.6
0.4
0.6
0.7
0.6
0.6
0.4
1.2
0.9
1.2
0.7
1.3
0.9
1.1
0.7
Na
meq/lOOg
0.3
0.3
0.4
0.4
0.3
0.6
0.5
0.4
0.3
0.7
0.5
0.2
0.1
0.8
0.7
0.4
0.1
Organic
Matter
%
7.2
7.2
3.7
2.0
1.4
7.0
5.5
1.7
0.8
5.7
5.0
2.9
0.9
5.4
4.1
2.4
0.8
P
17
16
9
4
5
34
16
7
4
65
17
13
13
89
32
21
5
K
150
140
70
48
33
180
94
55
32
350
230
58
24
330
230
110
37
Ca
ppm •-
3100
3000
2300
1900
1800
2400
2300
1900
1800
3000
2900
2100
1700
2900
2700
2100
1500
Mg
440
390
240
160
120
370
280
150
110
280
220
120
66
370
210
110
56
Zn
5.0
3.0
1.1
0.5
0.5
3.1
1.8
0.8
0.5
4.0
2.3
0.9
0.6
4.1
3.0
1.5
1.0
Fe
26
21
13
6
4
17
13
6
4
29
22
11
4
32
36
25
10
-------
wastewater was abundant in K, and increases in absolute amount were substan-
ial in the top 60 cm. The highest amount, 350 ppm would be considered "very
high" by most standards; e.g. Oregon uses 560 kg/ha of available K as the
value separating "high" and "very high", and 350 ppm converts to about 780
kg/ha in the plow layer. High soil K should have little adverse effect on
soil characteristics or plant growth, and is mainly reflected in K concen-
tration of forage.
Zinc (Zn) was the only "heavy" metal contained in the wastewater in
significant amounts. The upper 30 cm of soil showed some tendency to accu-
mulate available Zn, but deeper soil layers increased relatively more.
Available iron (Fe) increased at similar or greater relative rates than Zn.
31
-------
SECTION 6
AGRONOMIC STUDY
INTRODUCTION
Land application of sewage effluent through crop irrigation is rapidly
becoming a popular method of cleaning up undesirable wastewater since crop
species can benefit from the available nutrients. Difficulty still exists,
however, in selecting crop species suited to a wastewater irrigation system.
The adaptability of a species depends to a great extent on climatic factors
as well as the operation of the system, the nature of the waste, and the
intended use of the harvested crop.
The purposes of this study were: (1) to use field plots to determine
the viability of the species under the harsh environmental conditions, and
(2) to use controlled environmental experiments to study the effects of the
cheeseplant effluent on forage growth and quality.
FIELD STUDY
Quality factors of the seventeen forage species harvested in 1976 are
listed in Table 10. The species were harvested before flowering with the
onset of frost. No yield data were collected as the spray system was not
operational the first part of the growing season. These quality factors
appear to be in the range for acceptable livestock feed (Morrison, 1958).
The protein percentages of the grass species were slightly higher than those
grown in the controlled environment study. This could be due to the fact
that the field plants were harvested before flowering. The in vitro dry
matter digestibility (IVDMD) results were lower than was observed in the
growth chamber and greenhouse; however, some of the same trends were observed.
Sainfoin had a low IVDMD in both the field study and the controlled environ-
ment studies. The sainfoin IVDMD data may be invalid as the steer from which
the rumen fluid was collected was on an alfalfa rather than a sainfoin diet.
Tall fescue and orchardgrass had the highest IVDMD of the grass species in
both experiments. The ash content of the legumes was lower than the grass
species. The legumes alfalfa and cicer milkvetch were superior in protein
content.
Table 11 shows plant tissue concentrations of N03, P, K, Ca, Mg, Na,
SO^, Fe, Mn, Zn, Cu, and B. The P percentages were higher than normal in the
grass species, unlike the controlled environment study, which could be ex-
plained by the early growth stage at which the field plots were harvested.
The NOs-N levels were well below the livestock toxicity level of .34 to .45
32
-------
TABLE 10. QUALITY FACTORS OF 17 FORAGE SPECIES FROM FIELD PLOTS.
HARVESTED AUGUST 27, 1976
Reed canarygrass
Smooth bromegrass
Meadow bromegrass
Tall fescue
Creeping foxtail
Alfalfa
Sainfoin
Creeping wildrye
Idaho fescue
Steambank wheatgrass
Cicer milkvetch
Basin wildrye
Western wheatgrass
Thickspike wheatgrass
Orchardgrass
Mountain bromegrass
Timothy
Protein
16.1
12.3
14.9
15.2
16.3
20.4
15.7
15.0
15.7
13.0
19.6
13.4
12.8
i
12.9
13.6
12.8
11.2
Fat
4.1
3.6
4.1
3.7
5.1
4.7
2.8
4.3
4.4
3.2
4.3
2.8
2.9
3.4
4.3
2.9
3.6
Percent
Fiber
22.1
31.2
27.0
23.4
20.5
14.2
20.8
23.0
23.0
28.1
16.3
27.6
30.0
32.0
27.2
30.1
34.0
Ash
12.1
15.8
10.2
12.0
12.5
9.4
8.2
11.5
14.9
13.7
11.3
10.3
12.0
11.1
13.1
10.0
8.7
IVDMD
68.72
65.19
68.58
71.44
68.65
68.00
64.35
61.78
63.87
62.43
70.15
62.18
64.66
59.78
71.52
70.23
61.99
33
-------
TABLE 11. CHEMICAL COMPOSITION OF 17 FORAGE SPECIES FROM FIELD PLOTS
HARVESTED AUGUST 27, 1976
Percent
Reed canarygrass
Smooth bromegrass
Meadow bromegrass
Tall fescue
Creeping foxtail
Alfalfa
Sainfoin
Creeping wildrye
Idaho fescue
Streambank wheatgrass
Cicer milkvetch
Basin wildrye
Western wheatgrass
Thickspike wheatgrass
Orchardgrass
Mountain bromegrass
Timothy
N03-N
.039
.034
.038
.046
.042
.045
.030
.052
.038
.029
.054
.041
.029
.027
.047
.043
.033
P
.38
.34
.32
.37
.37
.25
.29
.34
.32
.26
.38
.30
.22
.23
.42
.33
.24
K
2.8
2.0
2.6
2.7
2.6
2.0
1.8
2.7
1.6
1.2
3.5
2.2
1.4
1.1
2.8
2.6
2.1
Ca
.56
1.0
.52
.55
.70
1.7
1.8
.65
.71
.83
1.2
.54
.57
.56
.53
.65
.44
Mg
.26
.50
.22
.24
.28
.37
.31
.25
.33
.26
.32
.24
.18
.22
.29
.23
.19
Na
.08
.10
.06
.15
.17
.23
.16
.15
.09
.08
.19
.13
.11
.11
.10
.09
.07
S0i»
.09
.10
.06
.07
.11
.12
.13
.10
.07
.08
.06
.05
.04
.05
.11
.07
.06
Fe
150
1500
450
140
440
210
170
500
1200
1300
520
540
450
700
300
320
240
Mn
40
120
64
60
96
33
56
59
61
65
51
42
40
33
61
52
46
ppm
Zn
18
121
20
15
29
23
23
24
19
16
27
22
13
13
17
23
26
Cu
2
4
4
2
4
6
5
4
4
2
6
2
1
2
3
6
3
B
3
5
3
5
2
10
13
2
3
4
15
4
5
4
4
3
4
-------
percent. Smooth bromegrass had a considerably higher concentration of Fe and
Mn than any of the other species. Alfalfa and sainfoin had higher percent-
ages of B, Ca, and S than the grass species. Overall, these concentrations
do not appear to be either toxic or deficient.
Since the plots were only consistently watered for approximately two
months before harvest, it would be difficult to observe any toxicities
or deficiencies which might occur in the forage plants or the soil. Several
years of effluent irrigation on the plots would be necessary to indicate if
the chemical composition of the plants was going to change significantly.
Plant survival under the ice pack during the 1976-77 winter was very
poor. Garrison creeping foxtail, reed canarygrass, smooth bromegrass, and
western wheatgrass were the only species which maintained an adequate stand
in 1977- The forage yield and quality of these four species are shown in
Table 12. The two highest yielding species were Garrison creeping foxtail
and reed canarygrass. These two species were similar in quality with the
exception of mineral content and IVDMD in which Garrison creeping foxtail
was higher in quality. In terms of feed for livestock the 13% higher IVDMD
for creeping foxtail would make this species far superior for use as a peren-
nial forage on a high altitude disposal site. The second cutting of creeping
foxtail was not harvested because of poor water distribution; however, where
it did receive water, its regrowth was considerably greater than that of
reed canarygrass.
Western wheatgrass, although it was low in yield, had a superior N-free
extract (NFE). It was also more digestible than reed canarygrass and con-
tained more favorable N03-N and crude fiber than the other species. The
mineral content of western wheatgrass was less than the other species.
Smooth bromegrass had the highest level of digestibility of the four
species; however, it also had a less favorable NOa-N content. The NOs-N
contents of Garrison creeping foxtail, reed canarygrass, and smooth brome-
grass were near the toxic level for livestock.
A harvest date study on reed canarygrass was conducted to define a
schedule which would result in forage palatable to livestock. Sufficient
growth to allow adequate nutrient uptake was also a consideration. The reed
canarygrass was in the preflower stage at the time of the first harvest on
July 7, 1977. The plots harvested on July 7 were again harvested September
13. The regrowth which occurred during the 78 days following the first har-
vest was small as indicated by the forage yield (Table 13). The yield of
the single harvest on September 13 was significantly greater than the total
yield of the two cut system. However, the forage IVDMD mineral content, and
P content from the one harvest at the end of the growing season were signifi-
cantly lower than that of the two cut system. In most cases the forage
quality of the second cutting was superior to the two first cutting treat-
ments. The NOs-N content of the July 7 harvest was within the toxic range
for livestock.
Spring barley was not adapted to the sprayfield environment. Very poor
seed germination and slow plant development was observed.
35
-------
TABLE 12. FORAGE QUALITY AND YIELD OF FOUR FORAGE SPECIES WHICH SURVIVED THE FIELD CONDITIONS.
HARVESTED JULY 30, 1977
Species
Protein
Fat
Crude
Fiber
IVDMD
Ash
NFE
Ca
P
N03-N
Forage
Yield
Garrison
Creeping Foxtail
Reed canarygrass
Smooth bromegrass
Western wheatgrass
16.6 a* 3.8 a 31.7 a 45 b 11.6 a 36.3 b
16.4 a 3.2 a 33.4 a 32 c 9.6 b 37.4 b
20.8 a 3.5 a 30.4 ab 52 a 9.6 b 35.6 b
18.2 a 3.6a 28.4 b 44 b 8.9c 41.0 a
Kg DW/ha
.42 a .32 a .29 a 8415**
.41 a .32 a .29 a 8585
.66 a .28 a .32 a 4115
.46 a .25 a .14 b 3775
* Means within a column followed by the same letter are not significantly different at the .05
level according to Duncan's New Multiple Range Test.
** Forage yield was not statistically analyzed due to an uneven sprinkler pattern in the plot area.
Quality samples were taken from adequately watered portions of the plots.
-------
TABLE 13. FORAGE QUALITY AND YIELD OF REED CANARYGRASS FROM A ONE-AND TWO-CUT HARVEST
SCHEDULE AT THE DISPOSAL SITE
Crude
Harvest Date Protein Fat Fiber IVDMD Ash NFE Ca P N03-N Yield
Kg DW/ha
/o "' " ~~~~ " "~
7/7/77 19..9 b* 3.22 b 30.5 a 48 a 11.05 b 35.2 ab .36 b .51 a -38 a 4950
(1st cut)
9/13/77 28.9 a 4.85 a 19.5 b 51 a 13.08 a 33.6 b .68 a .55 a .17 b 1112
(2nd cut of 77) 6062 b
9/13/77 17.4 b 3.35 b 30.3 a 40 b 9.38 c 39.6 a .36 b .36 b .20 b 8932 a
* Means within a column followed by the same letter are not significantly different at the .05 level
according to Duncan's New Multiple Range Tests.
-------
CONTROLLED ENVIRONMENT STUDY
The highest dry matter production (mg/day) in the grass species was
obtained with the control treatment at both temperatures, although differ-
ences were not significant for smooth bromegrass and meadow bromegrass
(Table 14). The control solution, which was based on the fertilizer re-
quirement of the soil for forage production, contained significantly more
N and P than did the effluent or synthetic treatments (Table 1). The super-
ior growth by the control treatment suggested that N and P levels in the
effluent were not sufficient for grass forage production. However, the
growth rate of the legume species was not affected by irrigation treatment
(Greene, 1976).
Treatment effects on protein percentage were more evident in the grass
species than in the two legumes (Table 14). The effluent treated grass
species contained considerably less protein than the control at the 20/10°C
temperature, indicating a deficiency of available nitrogen in the effluent
treatment. To maintain adequate growth and nutrient uptake of grass species
at the Thayne disposal system, it may be necessary to add nitrogen. However,
the 1977 field data indicated that N was not limiting. Irrigation treatments
did not affect the protein percentage of the two legumes. The fact that the
forage yield and protein content of the two legume species were not reduced
by the effluent treatment indicates that legumes are better adapted to an
effluent disposal site than grass species if nitrogen is limiting. This
suggests that symbiotic dinitrogen fixation was sufficient and not affected
by the effluent.
Soil concentrations of nitrate generally decreased by the end of the
study from an initial value of 12 ppm (Fig. 9). This indicated that the
effluent was adding insufficient amounts of nitrate to the soil. However,
five of the seven species had a greater nitrate content in the soil when
irrigated with effluent than in either the control or the synthetic irrigated
pots. This suggests that these five species could not as efficiently utilize
the nitrogen contained in the effluent (including organic N) as that in the
control.
The P concentration of the plant tissue generally was not affected by
irrigation treatment. However, in tall fescue at the low temperature, and
reed canarygrass and meadow bromegrass at the high temperature, the effluent
treatment had a higher P content than the control (Table 14). Soil analysis
at the end of the experiment indicated that available soil phosphorus accu-
mulated during the study, since the soil initially contained 17 ppm avail-
able phosphorus (Fig. 10).
The percent IVDMD for all species was similar for the effluent and con-
trol treatments (Table 14). The synthetic treatment produced a significantly
lower IVDMD in creeping foxtail than the other two treatments at the cooler
temperature. Meadow bromegrass had a higher IVDMD at the high air tempera-
ture when it was watered with the synthetic as compared to the control.
Dry matter production was generally greater at the higher air tempera-
ture (Table 14). However, the growth rate of tall fescue was significantly
38
-------
TABLE 14. EFFECT OF THREE IRRIGATION TREATMENTS AND TEMPERATURE ON THE GROWTH,
IN VITRO DRY MATTER DIGESTIBILITY (IVDMD), PROTEIN AND PHOSPHORUS OF
SEVEN FORAGE SPECIES
tng dry wt/day % Protein
% Phosphorus
% IVDMD
Irrigation
Treatment 20/10C23/18C 20/10C23/18C 20/10C23/18C 20/10C23/18C
Control
Effluent
Synthetic
Sl.lat 57.6a
37.2b 39.7b
34.6b 31.2c
Reed canarygrass
7.9a 9.4a .09a
6.9b 10.6a* .09a
6.7b 9.9a* .07a
.12c 71.9a 73.Oa
.23a 72.9a 69.8a
.18b* 74.3a 70.4a
Smooth bromegrass
Control 34.9a 55.6a* 8.8a 9.7a .06a .26a*
Effluent 23.7a 30.Oa 7.1b 11.la* .09a .28a*
Synthetic 30.Oa 31.2b 6.8b 9.9a* .07a .21a*
74.9a 69.la*
71.9a 67.9a*
71.3a 70.3a
Control
Effluent
Synthetic
Control
Effluent
Synthetic
Control
Effluent
Synthetic
Control
Effluent
Synthetic
Control
Effluent
Synthetic
36.5a
35.4a
25.5a
30.5a
21.6b
12. Ob
45. la
51. la
41.6a
53.7a
64.6a
53.2a
56.8a*
37.4ab
15.6b
51.2a 56.8a
31.Ib 37.4b
24.7b 15.6b
49.7a*
29.7.b
19.4b
105.6a*
lll.Sa*
92.9a*
120.Oa*
117.9a*
105.6a*
Meadow bromegrass
9.2a 12.la .10a .23b
6.Sab 12.2a* .lla .34a*
7.5b 10.5b .10a .12c
6.6a
5.3b
4.5b
7.8a
7. lab
6.3b
15.4a
16.8a
17. la
l
13.4a
13.2a
13.2a
Tall fescue
10.3a* .07b
10.2a* .15a
10.7a* .09b
Creeping foxtail
9.9a* .10a .19a
10.2a* .05b .28a*
9.0a* .09a -20a*
Alfalfa
19.6a* .03a
20.3a* .03a
20.7a .04a
Sainfoin
19.3a* .10a
18.4a .lla
18.7a* .09a
76.la 71.Ib
73.9a 72.lab
73.3a 76.6a
.27a* 78.la 73.2a
.29a 77.0ab 72.5a
.23a* 73.7b 76.5a
71.3a 70.8a
71.la 71.6a
64.8b 70.la
.21a* 79.Oa 75.3a
.16a 78.4a 76.6a
.21a 79.9a 76.4a
.22a*
.21a
.22a
t Species means within a column and followed by same letter are not signifi-
cantly different at the .05 level according to Duncan's Multiple Range Test.
* Differs significantly from 20/10C value according to the t-test at the .05
level
39
-------
Synthetic
14
12
10
4-1
•H
2
co
CO
CO
M
60
0) OJ
rt u
CO
co
CO
i-l
42 00
4-1 CU
o e
o o
e M
co pa
CO
co
co
M
& 00
O 0)
TJ B
CO O
CU M
cu
3
iH O
rH CO
CO CU
H Pn
00
0 rH
•H -H
a. co
0) 4J
cu x
rJ O
O Pn
CO
M-l
e
•H
O
M-l
.5
CO
Figure 9. Soil nitrate concentrations for seven forage species irrigated with
three treatments under controlled environments at the conclusion of
the study. Initial concentration was 12 ppm
-------
Synthetic
£
PH
1-1
o
P,
co
o
A
PH
50
40
30
20
10
CO
CO
to
^
M
T3 CO
cu a
cu to
ctf o
] Effluent
KXXXXN Control
CO
CO
cd
n
fi 60
4-J CU
o g
o o
S n
W pq
CO
CO
is
o
T3
01
CO O
CU M
0)
3
rH o
rH CO
CO CU
H fn
C iH
•H -H
d, CO
CU 4-1
CU X
M O
U PLI
CO
m
tH
CO
U-(
H
<
C
•H
O
M-l
CJ
•H
CO
CO
Figure 10. Soil phosphorus concentrations for seven forage species irrigated
with three treatments under controlled environments at the conclusion
of the study. Initial concentration was 17 ppm.
-------
higher at the cooler than the warmer temperature when it was watered with the
synthetic treatment. The growth of reed canarygrass was not significantly
affected by temperature, although it was the highest yielding of the grass
species at both temperatures. This response is in agreement with other
studies which have shown reed canarygrass adapted to land disposal systems
(Sopper, 1973). The percentage increase in yield of alfalfa and sainfoin
with the higher temperature was much greater than' for the grasses.
The protein content of forage when watered with effluent was signifi-
cantly higher for the 23/18C air temperature for all species. Consequently
the reduced protein level at the 20/10C temperature significantly lowered
the feed value of the forage for livestock. The problem of low protein con-
tent with the use of effluent under high altitude conditions would be less-
ened if a legume were grown rather than a grass, but more of the grasses
tested survived the field environment.
The forage produced under the low temperature regime generally had less
than one half the phosphorus content of forage in the high temperature
regime. In general, the forage from all species tested and grown under the
low temperature would have to be supplemented with phosphorus when fed to
most classes of livestock.
Smooth bromegrass was the only species in which IVDMD was significantly
affected by temperature. The IVDMD of smooth bromegrass was reduced by the
high temperature when watered with both the effluent and the control
treatment.
In summary the response of the grass species to the effluent and synthe-
tic irrigation treatments generally included reduced growth and protein. The
percent P and IVDMD were not usually affected by the effluent. Legumes
treated with effluent produced growth rates, protein content, P content and
IVDMD which were comparable to the other treatments. Apparently there were
no constituents of the effluent which significantly reduced growth, since it
was not observed that plants watered with the synthetic effluent containing
only N, P and K yielded more than those watered with the effluent. It
appears that temperature may be the limiting factor in the high altitude
effluent disposal system at Thayne, Wyoming. At the low air temperature,
limited growth may limit the uptake of nutrients necessary for acceptable
crop quality and, in some cases, yield.
SUMMARY
Two controlled environment experiments and the field plots were used to
evaluate seven forage species for growth, quality and adaptability to cheese-
plant wastewater under high altitude conditions. Ten additional species
were also evaluated in the field.
The controlled environment experiments indicated that there could be a
deficiency of nutrients in the effluent to adequately produce good quality
forage. The control treatment tended to have better growth and quality
characteristics than plants treated with effluent or a synthetic effluent,
42
-------
although it was not as apparent at the warmer temperature. When the plants
were subjected to a warmer environment, deficiencies of N and P were not as
evident indicating that temperature may be a limiting factor for adequate
availability and uptake of nutrients. The legumes showed more potential for
taking up P than the grass species. Soil data showed that N was being de-
pleted from the soil while P was accumulated.
The forage harvested from the field plots in 1976 did not show any ad-
verse effects of wastewater on quality factors or chemical composition of
the species studied. Although nitrogen existed in low concentrations in the
effluent, no deficiencies existed in the plant species indicating that there
was adequate nitrogen in the soil.
Four of the seventeen forage species survived the sprayfield ice pack
which resulted from the 1976-77 winter. The 1977 yields of Garrison creep-
ing foxtail and reed canarygrass were sufficient to consider them adapted to
the sprayfield environment. The forage quality of Garrison creeping foxtail
was superior to that of reed canarygrass. Both species produced forage
sufficiently high in NOs-N to be potentially toxic to livestock.
The regrowth of reed canarygrass which followed the first harvest was
very poor although the cutting regime resulted in higher quality forage.
The total season yield of a two-cut system was significantly lower than that
of a single harvest at the end of the growing season.
43
-------
SECTION 7
TREATMENT OF WASTEWATER IN A SPRAYFIELD ICE PACK
INTRODUCTION
While disposal of wastewater effluent on land is generally practiced
during the growing season, in some situations it may be desirable to apply
the effluent during the winter as well as the warmer growing season. Such a
case existed at Thayne, Wyoming. Due to the continuous high volume of
liquid waste from the cheese plant (approximately 1325 m3/day), the small
tax base of Thayne, and the scarcity of land available for a larger land
treatment system, it was considered to be economically prohibitive to build
a system utilizing wintertime storage lagoons. For this reason, effluent
is applied to the sprayfield throughout the entire year, regardless of the
weather conditions. This results in the formation of an ice pack on the
sprayfield during the winter months. It is the effectiveness of the ice
pack to renovate the wastewater that will be evaluated in this section.
SAMPLING
As the ice pack is formed, it generally allows the ground surface to
remain unfrozen with percolation of the melting ice pack into the soil
throughout the winter (Bunk, 1976 and DeVries, 1972). The ice pack acts as
an insulator trapping soil heat beneath the pack. However, the soil does
not remain unfrozen underneath the ice pack consistently. The 1976-77 win-
ter was dry (1.3 cm of natural precipitation for November and December) with
relatively warm days (see Fig. 19 & 20). The lack of natural precipitation
in the form of snow on the sprayfield and the warm temperatures influenced
the rate of build up of ice. As a result, spray applied on relatively warm
days melted any ice or snow which may have accumulated on the field. The
end result was a lack of ice cover on the sprayfield in November and the
first part of December, which allowed the uninsulated soil to freeze. As a
consequence, the soil did freeze down to the 50 cm level by the end of
December. From discussions with residents, the soil will freeze on the
average of once in ten years under normal snow conditions. Data on soil
temperatures are not available for a precise estimation.
Samples were taken from the ice pack in February, March, and April of
1976 and January through April in 1977. The ice pack was sampled in the
following manner: between three sprinkler laterals, samples were taken at
25 percent spacings between laterals and at 25 percent spacings between
pairs of sprinkler heads (see Fig. 11). Eight sampling points perpendicular
to the three laterals were used for each sampling date with the transect
44
-------
I _ I January sampling points
February sampling points
Z\ March sampling points
\_/ April sampling points
X ^S
v,, x^
n n a c
o o o c
A A A 4
C 0 O O £
^ Sprinkler ^
< — Lateral
3
) D n n c
* o o o c
y A A A 2
j^
o o o <:
x
"X
]
)
£
>
Figure 11. Location of ice pack sampling points.
45
-------
moved parallel to the lateral each month. At each sampling point, four holes
were bored to the soil surface with the core of ice between the four holes
removed. From this core of ice, composite samples were made for each 25 per-
cent of depth (see Fig. 12). For example, for a 120 cm hole, composite sam-
ples were made of each 30 cm section. This method of sampling tended to
provide ice of similar ages at each sampling depth for all holes regardless
of the relative thickness of the ice pack.
Bucket lysimeters were also placed in the sprayfield in clusters (see
Fig. 13). Ice pack melt water percolated down into the lysimeters and was
trapped in the buckets which were designed to collect percolate from several
soil depths.
ANALYSES OF SAMPLES
All water samples were analyzed for 5-day biochemical oxygen demand
(BODs), chemical oxygen demand (COD), nitrite (NOj), nitrate (N03), ammonia
nitrogen (NHa), total Kjeldahl nitrogen (TKN), and fecal coliforms. These
samples were analyzed according to "Standard Methods" (1971) after being
preserved in the field and transported according to Environmental Protection
Agency recommendations for sample preservation (EPA, 1971), with the excep-
tion where samples were collected for coliform analyses. Coliform analyses
of liquid samples withdrawn from lysimeters were begun immediately in the
field while ice pack samples were transported in a frozen state to Laramie
for analysis. Ice pack samples of similar depth spacings were composited
for each sampling date. The water quality data from the ice pack are pre-
sented in Tables 15 and 16.
DISCUSSION OF RESULTS
The physical process of ice metamorphism results in a change in the
nature of the ice pack with time as more and more wastewater is applied
and the ice becomes thicker. The process of metamorphism begins with
the freezing of the sprayed effluent, due to simultaneous heat and mass
transfer with the atmosphere, as it contacts the air during spraying. When
the effluent freezes, the liquid forms crystals of almost pure water while
the dissolved and suspended matter in the effluent is distributed in cells
between the crystals forming pockets of concentrated impurities in the ice
pack (EPA, 1971, ). The pockets will have a lower freezing point due to the
salts present in them. When air temperatures are low, the ice crystals are
formed rapidly and tend to be very small. This causes the ice pack to ex-
hibit a low permeability which impedes the downward percolation of the un-
frozen pollutants in the ice pack.
The application of wastewater is continuous on a periodic basis during
cold periods with continual transmission of pore water to the soil beneath
the ice pack. After the liquid is deposited and frozen, there is a tendency
in thermal metamorphism for each crystal to reduce its surface area. A
fundamental consideration of thermodynamics is that a system at a fixed
level of entropy will seek the lowest level of internal energy. An ice pack
46
-------
* •-;• f It-
Figure 12. Sampling of ice pack.
is no exception. If the crystals grow, the resulting surface area per unit
mass is decreased so the internal energy of the system is reduced. In addi-
tion, surface curvature increases as energy is reduced resulting in a round-
ing of the ice crystals with time. This reduction of surface area per unit
mass causes an increase in the permeability of the ice pack since ice cry-
stals become coarser and pore spaces partly occupied by pollutants become
larger. The process of ice crystal growth is sometimes called destructive
or equi-temperature metamorphism (Bader, 1954; Ellmore, 1968; Gerdel, 1954;
Summerfield and LaChapelle, 1970; USAGE, 1956).
Investigations of the temperature profile of an ice pack have shown the
ice pack to possess a thermally active layer with diurnal variation existing
from the surface to an inversion layer. From the inversion layer to the
soil-ice interface, a negative and almost constant linear temperature gra-
dient exists with temperatures at the inversion layer of about -8°C to
temperatures of 0° to 2°C at the soil-ice interface. This temperature
47
-------
Sprinklers
Laterals
Figure 13a. Location of lysimeters between laterals.
Ground Surface
Soil Support Plate
Bottom is open
" 30.5 cm
Sampling Tube
Trough
Figure 13b. Detail of typical 15 centimeter lysimeter.
48
-------
TABLE 15. WATER QUALITY DATA FOR ICE PACK AT THAYNE, WYOMING ~ 1976
vo
Top 25 percent
February
March
April
2nd 25 percent
February
March
April
3rd 25 percent
February
March
April
Bottom 25 percent
February
March
April
Influent
January
February
March
April
BOD 5
mg/1
244
173
429
139
129
104
113
125
94
144
119
228
617
330
324
330
COD
mg/1
965
5,105
8,685
1,110
845
835
1,045
835
980
2,000
l',600
6,700
—
18,000
19,000
13,000
TKN
mg/1
3.2
8.2
32
3.5
7.5
6.6
3.5
6.6
5.5
5.4
16.6
33
14
8.4
28
7.2
NH3
mg/1
0.1
0.1
23
0.0
0.3
4.8
0.0
0.2
3.9
0.0
0.3
30.0
0.9
0.0
4.9
0.0
N02
mg/1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
NO 3
mg/1
1.2
0.5
0.2
0.9
0.2
0.2
0.6
0.4
0.2
1.3
0.4
0.4
0.6
0.6
1.2
0.4
Total Fecal
Phosphate Coliform
mg/1 #/100ml
0
63
0
0
825
88
0
1,038
1,338
350
2,713
4,575
— —
18,200
30,000
1,000
Specific
Conductance
y mhos /cm
143
175
—
—
75
—
81
85
— —
128
50
— —
670
375
925
1,100
-------
TABLE 16, WATER QUALITY DATA FOR ICE PACK AT THAYNE, WYOMING — 1977
Ul
o
Top 25 percent
January
February
March
April
2nd 25 percent
January
February
March
April
3rd 25 percent
January
February
March
April
Bottom 25 percent
January
February
March
April
Effluent
January
February
March
April
BOD 5
mg/1
65
234
640
4,600
23
196
524
1,200
65
156
430
3,300
62
210
520
1,000
610
1,252
640
565
COD
mg/1
760
1,000
94
—
1,200
260
210
—
1,200
260
210
61
1,400
490
370
—
280
2,200
2,600
43
TKN
mg/1
30
33
13
48
35
23
15
—
19
18
13
16
43
30
15
—
87
42
8.5
5.1
NH3
mg/1
1.9
6.5
1.1
— —
1.4
0.0
1.0
—
6.0
0.0
1.1
6.1
6.0
0.0
0.7
—
4.2
0.0
0.9
0.0
N02 NO 3
mg/1 mg/1
<0.1 0.3
<0.1 0.6
<0.1
— —
<0.1 0.4
<0.1 0.3
<0.1 0.2
—
<0.1 0.5
<0.1 0.1
<0.1 0.7
<0.1 0.0
<0.1 0.3
<0.1 0.1
<0.1 0.1
— —
<0.1 0.3
<0.1 2.3
<0.1 4.4
<0.1 7.1
Total Fecal
Phosphate Coliform
mg/1 #/100ml
2.5
0.6
0.1
—
—
2.3
1.8
2.4
—
1.3
0.48
—
2.4
1.7
—
—
2.1
1.5
—
0
18
0
40
—
220
0
40
0
160
0
1
0
93
0
—
3,000
12,800
100,000
0
Specific
Conductance
y mhos/cm
—
600
524
—
—
360
—
—
—
200
520
—
—
310
260
—
—
—
1,300
-------
gradient is approximately what would be expected at Thayne where the soil
generally does not freeze during the winter. The soil does not normally
freeze under a deep ice pack of 0.9m or more (Bergen, 1968).
It has been suggested that during the coldest parts of the winter, the
ice on the surface of the ice pack has a higher concentration of pollutants
than the ice lower in the pack (Stinson, 1974). The ice below the surface
of the ice pack appears to be insulated from the atmosphere by the surface
ice. Since the ice below the surface is insulated, ice crystals are able
to grow and the pollutants excluded from the nearby pure ice crystals in a
brine-like solution, are able to drain from the pack. This results in the
ice just below the surface being the purest. Ice at the surface has just
received new pollutants and has not had the opportunity to drain. Ice near-
est the bottom of the ice pack will demonstrate an increasing concentration
of pollutants accumulating at the soil ice interface, a phenomenon probably
due to the ice pack having a greater fluid conductivity than the soil just
below it, or, possibly, capillary action (Bergen, 1968; Colbeck, 1974;
Devries, 1972; EPA, 1971; Hanes et al., 1965; USAGE, 1956).
The average density of the ice pack gradually increases throughout the
ice accumulation season. This happens via a melt-freeze type of metamorphism
in which the ice crystals become rounded and melt water is trapped between
the grains, increasing the density of the crystals upon refreezing (Leak,
1966 and Wakahama, 1960). The density of the melted water containing con-
taminants is higher than the density of the ice. Therefore, it tends to
drain from the pores and gradually percolate through the permeable ice by
gravity.
In the early spring, densification of the ice is accelerated and the
ice pack becomes heavy with gravitational water. The ice is relatively free
of pollutants except at the top and bottom. However, as the melting of the
ice pack begins at the surface, the melt water permeates downwards, and the
pollutants are flushed out along with those concentrated at the surface
(Ellmore, 1968).
The results of analyses on ice pack samples taken during 1976 and 1977
at Thayne support the contention that the pollutants concentrate in the
upper and lower parts of the ice pack as occurred in Ellmore*s desalination
experiments (Ellmore, 1968). It should be noted that during the 1977 winter
season the ground surface froze preventing movement of ice pack percolates
into the soil. In addition, the ice pack during the winter of 1977 (by
observation) had a density similar to water frozen in a freezer while the
ice pack during the 1976 winter season had the appearance of a snow drift.
The permeability of the soil and ice pack in 1976 was such that there was no
surface runoff from the soil or the top of the ice pack. In 1977, there was
considerable surface runoff from the top of the ice pack indicating a much
denser ice with a lower permeability.
Biochemical Oxygen Demand
The BOD 5 in the top 25 percent and the bottom 25 percent of the ice pack
was higher than that of the middle portions of the pack (see Tables 15 and
51
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16). A comparison of sprayfield effluent data with BOD5 data from the ice
pack indicates that there was a reduction of BOD5 within the ice pack itself
during the winter months. The high BODs during April, 1977 can be attributed
to an apparent discharge of high strength whey by the cheese factory—a
material not normally applied to the field.
There are two possible explanations for the reduction of BODs in the ice
pack. First, biological degradation of oxygen demanding organic matter
could be occurring. While biological activity within an ice pack may seem
improbable, it should be pointed out that active microorganisms have been
isolated from polar ice caps. Activity may be reduced in scale under extreme
cold conditions but can continue as long as free water remains available to
the microorganisms (Brock, 1969). The fact that ammonification of organic
nitrogen, a process generally due to biological action, also occurred in the
ice pack, lends support to the contention that the observed BODs reduction
could be due to biodegradation. A similar reduction in the BOD5 was observed
in a snow pack made from municipal sewage (Wright, 1976). A second possi-
bility is that the decrease in BOD5 could be for ammonia nitrogen. Levels
of ammonia nitrogen in the ice were found to be several times greater (up to
30 mg/1) than any level measured in the wastewater (up to 4.9 mg/1). Fur-
thermore, the high levels occurred during April, near the time of ablation,
when the possibility of surface runoff and/or groundwater pollution would
have been the greatest.
The nitrogen data suggests two very important points. First, ammonif lo-
cation of organic nitrogen was taking place in the ice pack. Ammonification
of organic nitrogen can occur by simple hydrolysis but this is generally
limited to amides and imides. Ammonification generally occurs biologically
with oxidative deamination being the most frequent mode of microbial attack
(Thimann, 1963). While deamination can occur by other pathways in the
absence of oxygen, these routes for degradation of organic nitrogen are
energetically less favorable. Thus, the occurrence of ammonification in the
ice pack is suggestive of a biological process occurring aerobically.
Secondly, it would appear ammonia nitrogen was more mobile in the ice
pack than organic nitrogen (TKN less the ammonia nitrogen). This was evi-
denced by the greater percentage of ammonia nitrogen which migrated to the
bottom of the ice pack in most cases where comparative data exists compared
to the percentage of organic nitrogen which migrated. For example, 48 per-
cent of the ammonia nitrogen reached the bottom quarter of the ice pack as
compared to 20 percent of the organic nitrogen in April 1976. This may have
been due to the physical size or the relative solubility of the organic
nitrogen matter in comparison to the ammonia nitrogen. The ammonia nitrogen
would be found in a soluble state while at least a portion of the organic
nitrogen was associated with suspended matter. Due to the permeability of
the ice pack (or lack of it), the ammonia nitrogen would be expected to
migrate more easily. According to Fick's First Law, large particles have a
slower diffusion velocity and lower rate of leaching (Morawetz, 1965). This
may help to explain the increased migration rate of ammonia nitrogen com-
pared to the organic nitrogen.
52
-------
Phosphate
No observable trend in phosphate levels with depth in the ice pack was
noted for 1977 data. Concentrations throughout the ice pack were in excess
of levels desirable for direct discharge to streams.
Fecal Coliforms
Since it is possible for pathogens to leave the sprayfield by deep per-
colation or as aerosols or mist, fecal coliforms were included in the analy-
sis program as indicators of potential travel distances for bacterial path-
ogens. Bacterial drift in the atmosphere was not monitored but samples were
taken from the ice pack itself.
The fecal coliform levels in the ice pack (Tables 15 and 16) show a
considerable reduction over effluent coliform densities. It is likely that
the cold temperatures combined with exposure to ultraviolet radiation as the
wastewater is sprayed onto the field could account for a high mortality in
the bacteria. During the winter of 1976, ice pack coliform densities in-
creased with increasing depth while in 1977 no trend with depth was observed
and, in addition, observed coliform levels were generally much lower through-
out the ice pack than in 1976. During 1976, a thick ice layer was formed
over unfrozen soil. The insulating effect of the ice layer allowed drainage
of soluble pollutants from the ice as has been previously discussed. How-
ever, in the case of bacteria, being the size of suspended matter, it is
likely that the coliforms would not drain completely from the pack due to
physical impedance of movement. During 1977, the ice formed was less per-
meable and the bacteria were immobilized at the surface and exposed to the
elements, resulting in a high mortality. Die-off is a complicating factor
since the process is time dependent and the bottom ice is the oldest. The
trend toward increasing numbers near the bottom of the ice pack in 1977
would be even stronger without die-off.
Two other factors should be noted. In no case were large concentrations
of bacteria found at the ice surface. It is likely that this is due in part
to a higher die-off rate at the surface. As the bacteria drained in 1976,
they became "Protected" from radiation, dessication, etc., by the ice layer
itself. It should also be noted that the increase with depth seen in 1976
could be due to reproduction within the pack. The bacteria would be sur-
rounded by small cells of liquid, high in nutrients, which might be a suit-
able growth medium. It has been shown that at low temperatures (4°C) coli-
form die-off rates are reduced under controlled laboratory conditions in
sewage (in the absence of UV radiation) compared to death rates at higher
temperatures (Hanes et al., 1965). However, no growth phase was observed
at 4°C as was seen at higher temperatures. In ice, where water is less
available than in 4°C liquid, it is not likely that significant reproduction
rates are occurring.
FATE OF ICE PACK MELT WATER
To determine the fate of the ice pack melt water, two types of ground-
water samples were taken. They were: (1) water trapped by bucket
53
-------
lysimeters that contained 15, 30, and 45 cm of soil, and (2) wells that
extended into the water table. Samples of water taken from these sources
have shown that after three consecutive years of spraying wastewater on the
field and with a buildup of the ice pack each winter, no significant amounts
of pollutants have reached the groundwater.
An examination of the water samples from wells at the edge of the spray-
field did indicate that the total dissolved solids (IDS) increased from
approximately 300 mg/1 above the field to 1200 mg/1 below the field. Better
than 90 percent of the increase could be accounted for by increases in cal-
cium, magnesium, and bicarbonate ions. This increase was not unexpected
since passage of water through similar soils would be expected to increase
the TDS by leaching in approximately the same magnitude. A definite cal-
careous layer of soils exists in the sprayfield at depths of 45 to 60 cm,
which may account for the build-up of calcium, magnesium and bicarbonate in
the groundwater. All pollution parameters studied (BODs, nitrate, ammonia,
COD, total phosphate, and fecal coliforms) were either absent or were approx-
imately at the same concentrations as the groundwater from wells upstream
from the sprayfield. It should be noted that the groundwater samples from
the wells were taken from the top of the aquifer and were not homogeneous
water samples from the aquifer. Also the results do not preclude the possi-
bility that pollutants may reach the wells at some time in the future or
that other pollutants, not studied, are already reaching them. However,
since the pollutants examined encompass both conservative and nonconserva-
tive materials and living matter, none of which reached the wells in levels
significantly above background, the possibility of pollution occurring seems
remote. Other sites would require a case-by-case examination.
The lysimeter study was carried out during the winter of 1975-76 with
the purpose of gaining some insight into the renovation of the wastewater in
the soil matrix during the winter months. Additional studies are needed for
definitive statements but the preliminary results are of interest as they
relate to the renovation of the wastewater in the ice pack.
Nitrite nitrogen and ammonia nitrogen were found in small quantities in
the drain water (maximum of 1.8 mg/1 of NHs and 0.1 mg/1 of NOa) at soil
depths up to 45 cm in the soil. No change in TKN was found by the well
data over background groundwater samples. Thus, while TKN was decreasing
with depth, nitrate nitrogen was increasing. This suggests quite strong-
ly that the process of nitrification was taking place in the soil especially
in the upper soil strata. Nitrification is an aerobic, thermally sensitive,
process which might lead to the conclusion that it is unlikely to occur in
soil covered by several feet of ice. The presence or absence of oxygen in
the water in the lysimeters or soil was not examined but it should be re-
called that ammonification did occur in the ice pack and the process was
most likely due to oxidative deamination. This would lend evidence that the
ice pack, at least, was aerobic. Air was able to reach the storage cell of
the bucket lysimeter in small quantities during sampling which might have
allowed nitrification to occur in the bucket itself. However, limited use
of suction lysimeters during the winter of 1977 showed similar results.
This type of lysimeter samples the soil directly by suction of pore water
54
-------
and does not provide sufficient contact time with air to permit nitrification
to occur.
Samples from wells and springs adjacent to the field showed that neither
nitrite nor nitrate were reaching the wells or springs (Table 17). In addi-
tion, an agronomic study of the soils in the sprayfield showed that nitrogen
was being depleted from the soil. Also, the decline in soil ammonia nitrogen
in the lysimeters could not be accounted for by observed increases in nitrate
concentrations. This would suggest that denitrification may also have been
occurring simultaneously with nitrification in anaerobic microenvironments
within the soil matrix. This is not surprising since soil environments are
typically nonhomogeneous on a micro scale (Stevens, 1972).
Even during the winter there were significant reductions of BOD5 and COD
in the upper 45 cm of the soil mantle. An 80 percent reduction was found for
BODs, while COD had a 45 percent reduction. These decreases were probably
contributable to filtration of the organic matter by the soil as well as an
indication that some biological processes were occurring during the winter.
CONCLUSIONS
Knowledge of the changes taking place in an ice pack formed by the win-
ter application of wastewater to land using spray irrigation, will enable
better management of these types of systems. However, the data base for
this study is very limited and the results should be taken as cursory. From
the study at Thayne, Wyoming, the following conclusions can be made:
1. Formation of an ice pack can be used as a means of liquid storage
during the winter months as an alternative to the use of large holding
lagoons. This not only provides year-round use of the disposal facilities,
but also provides additional treatment.
2. It has been shown that anunonification occurred in the ice pack. At
the same time, nitrification was taking place in the soil mantle. Thus,
organic nitrogen was oxidized as it travelled from the surface of the ice
down into the soil, finally becoming nitrate nitrogen, its most oxidized
state. Although different reactions occurred in the ice and soil, they were
working in harmony to provide a, further treatment of the wastewater.
3. For the predominately cheese plant wastewater and this type of land
treatment system, there is little cause for concern of nitrate nitrogen con-
tamination of groundwater. Nitrate values during the test period were well
below federal drinking water standards (10 mg/1).
4. Ammonia nitrogen appears to be more mobile in the ice pack than
organic nitrogen.
5. The severe leaching of the soil by the applied wastewater will
increase TDS but will not increase BODs °r COD in the groundwater.
6. Due to differences in ice pack structure, particularly permeability,
55
-------
changes in water quality and in the soil mantle did not demonstrate the same
patterns from one year to the next.
56
-------
SECTION 8
MANAGEMENT AND DESIGN RECOMMENDATIONS FOR SPRAYFIEID
INTRODUCTION
To successfully treat wastewater, the process of planning, system design
and analysis, process design, construction, and operation and maintenance
must all be performed in a satisfactory manner. Unfortunately, this was not
the case at Thayne. With respect to this study, it was not the task of the
principal investigators to manage, manipulate, design, or plan the system,
but simply to monitor the system and give advice and suggestions when appro-
priate. Neither was it their task to pass judgement on any failure of the
Thayne system not directly related to the experimental aspects of the system.
Contained in this section are the recommendations on design and management
of the sprayfield based on research findings. The principal investigators
advise that these recommendations be considered for any land treatment
system operating on a year-round basis under high altitude conditions.
RECOMMENDATION FOR SYSTEM DESIGN
The sprinkler system is a buried solid set system with 24.4m by 24.4m
spacing. The pump was designed to deliver 47.3 liters/sec at a pressure of
483 Kpa at the sprinkler heads. Conventional horizontal impact sprinklers
were selected (Aqua Dial No. 53 with 0.48 cm X 0.64 cm nozzles). For the
given design pressure and spacings the application rate calculates to be 0.86
cm per hour. To determine the sprinkler systems uniformity of application,
the Christiansen Uniformity Coefficient (UCC) was determined at two loca-
tions. The UCC was 61 percent in the first test and 73 percent in the second
test.
According to Karmeli (1977) systems with a UCC less than 70 percent are
generally unsatisfactory for agricultural irrigation purposes (see Fig. 14).
The low UCC also means that approximately 40 percent of the area irrigated
received 1.1 times the average application rate or more and that 40 percent
of the area received approximately 60 percent of the volume of wastewater
applied. Given the low UCC and the high operation pressure of the system,
it is not recommended to operate the system anytime the average wind speed
exceeds 6.5 Km/hr.
There were no areas within the sprayfield not having sufficient moisture
for plant growth because of the sprinkler distribution pattern. However,
dry areas are unlikely to occur when the amount of wastewater being applied
57
-------
Figure 14. Sprayfield covered with ice, April 1977,
(Note the circles cut by the sprinkler
pattern—a symptom of poor uniformity
of application).
exceeds by 2 or 3 times the amount needed to bring the soil to field capa-
city. The one area that did lack water from time to time was the upper end
of the field. The end sprinklers were often plugged. This problem could be
prevented by adding cleanout valves at the end of the lateral and period-
ically flushing out the lines.
From monitoring the system at Thayne and comparing it to the sprinkler
systems used on irrigated farms, the following recommendations are made with
respect to sprinkler system design:
1. An economic optimization should be made between operational costs
(mainly energy) and capital cost in order to select optimum lateral and
sprinkler head spacings and operating pressure.
2. An analysis of wind speed should be made to make sure the system
can operate in all months with an acceptable uniformity of application. If
closer lateral and sprinkler spacings are required because of the wind, an
economic optimization should be made between sprinkler system cost and cost
58
-------
of additional storage needed to store water during prolonged periods of high
wind.
3. A cleanout valve should be placed at the end of each lateral.
4. All laterals and mains should be buried a sufficient depth to pre-
vent freezing. Soil should not be piled up over the pipes in lieu of a deep
trench. The piled soil prevents normal farming operations and the plants
that grow in these piles can cause odor and weed problems.
5. All laterals and mains should drain back to the pump wet well to
prevent any water in risers and sprinkler heads after the stoppage of
spraying.
6. All systems should meet existing agricultural standards for an irri-
gation system, especially in terms of uniformity of application.
MANAGEMENT OF SPRINKLER SYSTEM
Management of the sprinkler during warm weather should be conducted
similar to the agricultural sprinkler system. However, during the winter
months the system must contend with extremely cold weather. For example,
during January at Afton, Wyoming, there is a 0.43 probability that the mini-
mum daily temperatures will be below -18°C and the 0.06 probability that the
maximum daily temperature will be below -18°C, while the mean is -9°C. The
mean temperature at the sprayfield was -9°C for January, 1976 and -7°C for
January, 1977. Despite these cold temperatures only minor problems occurred
(see Fig. 15). The main reason for the successful winter time operation
was the relatively warm effluent temperatures. During January, 1976 water
temperature at the bottom of the holding lagoon was 5°C. The effluent is
pumped from the bottom of the holding lagoon.
As can be seen from Figure 16, ice will build up as high as the top of
the risers. The relatively warm water, however, will cut through the ice.
If a sprinkler head stops turning due to freezing, as they often do, the
stationary jet of water will hit the ice pack and spread as surface flow
before it freezes. The distribution of water on the ice pack when 50 percent
of the sprinkler heads were not turning appeared to be as good as when all
sprinkler heads were turning.
As was stated in Section 7, there were some problems with runoff from
the surface of the ice pack during the 1976-77 winter. This problem was
solved by the operator. Using the automatic controls, the water was
switched to a different part of the sprayfield every 15 minutes. During
ablation solution channels did develop through the ice pack due to the
frozen soil (see Fig. 17). This problem can only be solved by preventing
the soil from freezing in the fall.
59
-------
Figure 15. Severe build-up of ice around sprinkler head,
Figure 16. Ice build-up to top of riser.
60
-------
Figure 17. Solution channel in ice pack.
Based on two winters of observation, the following recommendations are
made with regard to winter management of the sprayfield:
1. The water in the holding lagoon should be maintained at 4°C or
above to prevent any serious build-up of ice on the sprinkler heads.
2. The set times should be 30 minutes or less to avoid excess melting
of the ice pack by the warm water and to prevent any possible runoff.
3. If cones of ice do develop around the sprinkler head, the head can
be removed temporarily allowing the warm water to melt the ice Immediately
adjacent to the riser (see Fig. 18).
4. An ice pack should be forced to form by spraying during the night
hours during the late fall when night-time temperatures are well below
freezing.
5. No more than two-thirds of the sprayfield should be used during the
winter. The remaining one-third of the sprayfield should be saved and used
in the spring at the time of ablation of the ice pack. If this procedure
is followed, no additional water will be added to the area under the ice
pack and water logging of the soil at the time of ablation can be minimized.
6. Following ablation of the ice pack, the irrigation schedule should
be returned to a summer-time mode. Any section of the sprayfield should not
be irrigated more than once per week. More frequent irrigations will keep
soil temperature low and retard plant growth.
61
-------
Figure 18. Melting of ice from around riser
by removal of sprinkler head.
'62
-------
SECTION 9
REFERENCES
American Public Health Association. 1971. Standard Methods for the
Examination of Water and Wastewater. American Public Health Association
New York, New York. 874 pp.
Analytical Quality Control Laboratory. 1971. Methods for Chemical
Analysis of Water and Wastes. Water Pollution Control Research Series
16020-07/71, U.S. Environmental Protection Agency, Cincinnati, Ohio.
298 pp.
Association of Official Agricultural Chemists. 1955. Methods of Anal-
ysis. Washington, D. C. 8th ed. 368 pp.
Bader, H. 1954. Snow and Its Metamorphism. Snow, Ice and Permafrost
Research Establishment, U.S. Corps of Engineers, Wilmette, Illinois.
30 pp.
Becker, C. F., and J. Alyea. 1964. Temperature Probabilities in Wyoming.
Bulletin No. 415, Wyoming Agricultural Experiment Station, Laramie,
Wyoming. 97 pp.
Becker, C. F., J. Alyea, and H. Eppson. 1961. Probabilities of Freeze
in Wyoming. Bulletin No. 381, Wyoming Agricultural Experiment Station,
Laramie, Wyoming. 16 pp.
Bergen, J. D. 1968. Some Observations of Temperature Profiles of a
Mountain Snow Cover. U.S. Forest Service Research Note RM-110, Rocky
Mountain Forest and Range Experiment Station, U.S. Forest Service, Ft.
Collins, Colorado. 7 pp.
Brock, T. D. 1969. Microbial Growth Under Extreme Conditions. In:
Microbial Growth, 19th Symposium of the Society for General Microbio-
logy, P. Meadow, and S. J. Pert, eds. Cambridge University Press,
Boston, Massachusetts, pp. 15-42.
Bunk, G. M. 1976. Renovation of Effluent in the Ice Pack and the Upper
Soil Mantle at a Wastewater Land Application Site. Master Thesis.
University of Wyoming, Laramie, Wyoming. 52 pp.
Colbeck, S. C. 1974. The Capillary Effects on Water Percolation in
Homogeneous Snow. Journal of Glaciology, 13: 85-97.
DeVries, J. 1972. Soil Filtration of Wastewater Effluent and the Mech-
anism of Pore Clogging. Journal of the Water Pollution Control Feder-
ation, 44(4): 565-571.
63
-------
Elmore, W. E. 1968. Water Purification by Natural Freezing. Master
Thesis. University of Wyoming, Laramie, Wyoming. 98 pp.
Fiske, C. H., and U. Subbarow. 1925. The Colormetric Determination of
Phosphorus. Journal of Biochemistry, 66: 375-400.
Georing, H. K., and P. J. Van Soest. 1970. Forage Fiber Analysis.
Agricultural Handbook 379, Agricultural Research Service, Washington,
D. C. pp 12-15.
Gerdel, R. N. 1954. The Transmission of Water Through Snow. Transac-
tions of the American Geophysical Union, 35(3): 475-484.
Greene, M. C., 1976. Effect of Cheeseplant Wastewater on the Growth
and Quality of Seven Forage Species Under High Altitude Conditions.
Master Thesis. University of Wyoming, Laramie, Wyoming. 53 pp.
Hanes, N. B., G. A. Rohlich, and W. B. Sarles. 1965. Effect of Temper-
ature on the Survival of Indicator Bacteria in Water. Journal of the
New England Water Works Association, 80(1): 21-28.
Kail, R. M., et al. 1972. The Effect of Date of Cutting on Yield and
Chemical Content of Ten Grass Species. Research Journal 63, Wyoming
Agricultural Experiment Station, Laramie, Wyoming. 21 pp.
Krall, J. L., et al. 1971. Evaluations of Sainfoin for Irrigated
Pasture. Bulletin No. 658, Montana Agricultural Experiment Station,
Bozeman, Montana. 19 pp.
Leaf, C. F. 1966. Free Water Content of Snow Pack in Subalpine Areas.
IN: Proceedings of the Western Snow Conference, Seattle, Washington,
34: 17-25.
Mehta, N. C., et al. 1954. Determination of Organic Phosphorus in
Soils: I. Extraction Method. Proceedings American Society of Soil
Science. 18(4): 443-449.
Metcalf & Eddy. 1972. Wastewater Engineering. McGraw-Hill Book
Company, New York, New York. 721 pp.
Morawetz, H. 1965. Macromolecules in Solution. John Wiley and Sons,
Inc., New York, New York. 495 pp.
Morrison, F. B. 1959. Feeds and Feeding. The Morrison Publishing
Co., Clinton, Iowa. 1165 pp.
Moyer, J. L., and W. J. Seamands. 1975. Tall Fescue. Bulletin No. 626,
Wyoming Agricultural Experiment Station, Laramie, Wyoming. 22 pp.
Richardson, L. R., and G. P. Roehrkasse. 1974. Alfalfa Variety Perfor-
mance Tests in Wyoming. Bulletin No. 609, Wyoming Agricultural Experi-
ment Station, Laramie, Wyoming. 22 pp.
64
-------
Seamands, W. J., and B. J. Kolp. 1975. Regar Bromegrass. Bulletin No.
625, Wyoming Agricultural Experiment Station, Laramie, Wyoming. 25 pp.
Sommerfeld, R. A., and E. LaChapelle. 1970. The Classification of Snow
Metamorphism. Journal of Glaciology. 9: 3-19.
Sopper, W. E. 1973. Crop Selection and Management Alternatives—
Perennials. Proceedings of the Joint Conference on Recycling Municipal
Sludges and Effluents on Land, Champaign, Illinois, pp. 143-152.
Stevens, R. M. 1972. Green Land—Clean Streams: The Beneficial Use of
Wastewater Through Land Treatment. Center for the Study of Federalism,
Temple University, Philadelphia, Pennsylvania. 329 pp.
Stinson, D. L. 1974. Atmospheric Freezing Pilot Test of Salt Removal
from Big Sandy River—Colorado River Water Quality Improvement Program.
Report for U.S. Bureau of Reclamation, University of Wyoming, Laramie,
Wyoming. 42 pp.
Thimann, K. V. 1963. The Life of Bacteria. Macmillian, New York,
New York. 775 pp.
United States Corps of Engineers. 1956. Snow Hydrology. North Pacific
Division of U.S. Corps of Engineers, Portland, Oregon. 437 pp.
Wakahama, G. 1960. The Role of Melt-Water in the Densification Pro-
cesses of Snow and Firn. The Institute of Low Temperature Science,
Hokkaido University, Sapor, Japan. 26 pp.
Wright, K. R. 1976. Sewage Effluent Turned to Snow. Civil Engineering-
ASCE, 46(5): 88-89.
65
-------
APPENDIX
I. RESULTS OF WATER QUALITY MONITORING
66
-------
TABLE 17. NUTRIENT AND BIOLOGICAL DATA FOR FOURTEEN WATER SAMPLING POINTS
ON
Location:
6-4-75
10-25-75
1-25-76
2-24-76
3-15-76
4-14-76
5-25-76
composite
5-26-76
9am -8 pm
5-26 5-27-76
9pm - Sam
5-27-76
9am - 8pm
5-27 5-28-76
9pm - Sam
5-28-76
9am - 8pm
5-28 5-29-76
9pm - 8am
5-29-76
9am - 8pm
5-29 5-30-76
9pm - Sam
Influent
NO 3 N02
mg/1 mg/1
0.5
5.1 0.5
2.0 0.5
<0.1
0.2 <0.1
1.0
0.5
2.3 1.0
0.5
2.7 1.0
3.9 1.0
0.2
0.1
6.9 1.0
NH3
mg/1
0.0
0.0
12
0.0
6.9
11
0.0
5.1
0.0
0.0
5.3
7.1
0.0
TKN
mg/1
0.7
1.1
97
2.5
34
62
3.4
30
2.1
1.8
22
33
0.9
Total Spec. Fecal
TOC BODs COD TSS POi, Cond. Coli.
mg/1 mg/1 mg/1 mg/1 mg/1 pH y mhos/cm No/100 ml
2.53 6.5 2,637
44 23 12 0.19
18 6.8 380
30 24 5.6 400 900
336 19,000 4.4 2,500 17,500
60 12,000 4.2 2,600 14,000
16,000
1,290 18,000
42 38
2-, 070 3,300
6 1,600
1,890 4,500
6 1,400
1,900
1,800
(continued)
-------
TABLE 17. (continued)
oo
Location: Influent (cont.)
Date
9-9-76
10-9-76
llr8-76
12-21-76
1-7-77
2-12-77
3-6-77
4-12-77
5-13-77
6-18-77
7-15-77
8-18-77
9-19-77
* Not run due
a >50,000
NO 3
3.6
6.5
0
4.8
0.1
0.6
4.4
4.5
4.6
3.2
0
0
N02 NH3
0.5 0.0
5.0 0.0
0 0
.5 0
0.6 0
0
0.9
1.0 0
<0.1 16
<0.1 1.8
<0.1 53
<0.1 5.4
TKN TOC
82 1,723
2.0 10
1.9 20
130
27 483
1.4
8.2
35
N 0
72
17
250
90
BOD 5
>1,500
1,500
5
570
620
320
211
295
SAMP
1,500
165
1,170
1,560
Total Spec.
COD TSS POij pH Cond.
17
15
21
5
1
2
1
L E
13
57
18
,000 616 2.53
,000 28 0.57
,000 20 0.96 7.5 458
,600 2.09
,200 160 2.9
0 12 0.4
,600 1.01 4.8 1,100
,900 1.76
,000 1,200
610 1.37 320
,000 * 5.2 2,400
,000 * 5.8 2,200
Fecal.
Coli.
>16,000
1,300
16,300
40,000
65,000
4,600
0
TNTCa
1.3xl06
980,000
1.3xl06
l.lxlO6
to interferences
(continued)
-------
TABLE 17. (continued)
Location: Aerated Lagoon
VO
Date
10-25-75
1-25-76
7-7-76
9-9-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
N03
0.2
5.5
2.9
.9
3.3
3.2'
2.3
0
0.2
Total Spec.
N02 NH3 TKN TOG BOD5 COD TSS PO^ pH Cond.
0.1 0.0 0.9 44
1.2
1.0 0.0 24 665
0.8 0 7.5 828
0.1 1.6 69
N 0
<0.1 1.6 120
<0.1 0.2 48
<0.1 1.8 77
<0.1 3.0 28
NA-* Not run due to interferences
a Too numerous to count, actually greater
have been subject to contamination.
b >50,000
1,500 72 2.0
615 6.4 475
0.2 7.5 460
>1,600 2,700 264 2.29
620 190 NA
155 4,300
SAMPLE
1,600 6,500 660
705 0 1.69 700
1,440 10,000 * 4.6 750
1,410 15,000 2.56 5.2 440
than 50,000, bottle froze and broke in transit,
Fecal
Coli.
<2
TNTC3
TNTCb
198,000
178,000
l.OxlO6
1.4xl06
sample may
(continued)
-------
TABLE 17. (continued)
Location: Effluent
•vl
o
Date
9-15-75
10-18-75
10-25-75
1-25-76
2-24-76
3-15-76
4-14-76
5-25-76
composite
5-26-76
9 am - 8 pm
5-26-76
9 pm - 8 am
5-27-76
9 am - 8 pm
5-27-76
9 pm - 8 am
5-28-76
9 am - 8 pm
5-28-76
9 pm - 8 am
5-29-76
9 am - 8 pm
5-29-76
9 .pm - 8 am
NO, NQ>
0.3
0.6
0.6 0.1
0.6 0.1
1.2 <0.1
0.4 <0.1
<0.1
<0.1
0.1
0.1
0.5
0.1
3.4 2.0
0.1
1.0
Nft
1.6
0.0
4.9
0.0
5.1
0.0
5.3
3.9
4.4
3.5
0.0
2.8
1.8
TKN
19
31
14
8.4
28
7.2
19
3.5
41
21
25
30
1.8
15
12
TOG BOD5
386
617
330
324
330
1,350
1,170
1,290
1,830
1,350
1,860
Total Spec .
COD TSS POf pH Cond.
180 2.4 6.5 693
370 3.1 5.1 989
8,000 100 2.7
2.8 775
18,000 7.3 375
19,000 4.1 925
13,000 4.2 1,100
2,500
2,900
2,800
2,900
2,900
3,000
2,900
29,000
24,000
Fecal
Coli.
18,200
17,500
(continued)
-------
TABLE 17. (continued)
Location: Effluent (continued)
Date
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
2-12-77
3-6-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
NO 3
3.0
0.0
0
0.9
0.3
2.3
4.4
7.1
2.4
1.2
0
0.1
N02
1
0
0
<0
<0
<0
<0
<0
<0
.0
.1
0
.5
.1
.1
.1
.1
.1
.1
NH3
3.0
1.8
0
0
4.2
0
0.9
0
11
39
31
29
TKN TOG
34 807
31 682
19 228
62
87 1,254
42
8.5
5.1
N 0 S
120
81
100
43
BOD 5
1,390
1,200
10
580
610
1,252
640
565
AMPLE
c
1,230
1,470
1,950
18
16
22
4
2
2
6
45
1
COD TSS
,000 52
,000 136
,000 194
,000
280 220
,200 120
,600
43
,800 240
0
,000
,500
Total Spec.
POi* pH Cond .
2.
2.
2.
2.
34
52
8 7.0 1,080
08
NA
2.
1.
2.
*
2.
1
48 4.5 1,300
27 1,250
4.2 1,000
93 5.0 320
Fecal
Coli.
>16,000
700
1,800
-------
TABLE ]?. (continued)
N>
jjucai
Date
10-25-75
1-25-76
2-24-76
3-15-76
4-14-76
6-23-76
9-9-76
10-19-76
11-8-76
12-21-76
1-7 '-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
.J.U11. U
NO,
3.7
2.9
2.4
4.8
5.5
0.8
0.5
3.6
1.2
2.1
0.1
0.1
0.0
0.0
0.0
0.1
ittuei. uj
NO,
<0
<0
<0
<0
<0
<0
<0
<0
<0
0
<0
<0
<0
<0
<0
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
ietj.it
NH3
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
1.4
0.0
0.0
0.0
TKN
5
0
1
0
1
0
0
0
2
0
4
1
1
1
0
.8
.7
.8
.7
.4
.7
.5
.9
.4
.7
.1
.7
.3
.1
.2
TOG BOD5
42
2
3
2
0
5 1.
8 9.
19 5.
16.5 6.
7.
15 5.
4.
7.
6.
6
2.
6.
3
5
9
2
3
9
6
0
4
2
5
COD
0.0
13
6.9
1.3
840
190
130
65
56
35
140
380
2,000
200
39
19
Total Spec.
TSS POit pH Cond.
8.0
6.9 400
7.4 375
7.5 400
7.5 400
0.0 0.12 7.3 481
0.33
0.61
0.44
0.03
NA
0.02 7.4 965
0.03
0.13 360
0.11 6.8 180
0.01 7.2 500
Fecal.
Coll.
0
0
4
0
11
2
196
102
38
56
0
0
1
1
0
(continued)
-------
TABLE 17. (Continued)
Location: Flat Creek
Date
10-25-75
1-25-76
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
NO,
4.5
5.5
2.1
3.7
3.1
4.7
7.0
4.7'
4.8
3.8
3.2
0.0
0.9
N02
<0
<0
<0
<0
<0
<0
<0
<0
<0
<0
<0
<0
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
NH3
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
TKN
0.4
0.0
0.3
0.6
3.4
0.4
0.0
ft
O.V"
0.0
3.7
0.9
0.4
0.9
TOG BOD 5
31
2
5 2
7.5 6
1.0 1
2.5 2
2
8 1
3
0
0
•
1
2
.4
.5
.2
.6
.4
.2
.0
.2
a
• •
.4
.0
COD TSS
0.0 0.0
980 40
170
36
6.4 26
0.0
84
7.4
1.8 6
1,900
130
4.2
3.1
Total Spec.
POM. pH Cond.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
05
7.6 360
10 7.4 458
03
22
05 8.0 416
09
06
02 7.9 412
01
05 280
03 7.4 265
02 7.2 300
Fecal.
Coli.
25
44
2
11
46
2
10
9
40
52
28
99
10
Lab error
(continued)
-------
TABLE 17 (Continued)
Location: Spring #1 (North)
Date N03 N02 NH3 TKN
10-25-75
1-25-76
2-24-76
3-15-76
4-14-76
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
4.3 <
4.0 <
3.3 <
4.3 <
6.6 <
1.2 <
1.5 <
3.6 <
0.0 <
0.1 <
2.1 <
0.1
0.5 <
0.3 <
0.0 <
0.0 <
:0.1
:0.1
:0.1
:0.2
••o.i
:o.l
:0.1
'•0.1
:o.l
:0.1
'-0.1
:0.1
:0.1
:0.1
:0.1
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.5
0.0
0.0
0.0
1.0
1.0
0.4
1.2
0.0
0.0
0.7
1.1
0.6
0.0
7.1
0.0
3.9
1.8
0.4
1.1
TOG BOD5
38
4.2
1.8
2.5
4 2
0 12
2.5 0.7
3.0 0.0
2.3
22 3.3
7.0
3.2
7.3
5.5
3.2
11.7
COD TSS
1.0 4.0
66
0.2
4.1
1,400 4.0
420
43
6.5
2.1
46
130
52 10
320
20
15
5.7
Total Spec.
P0i» pH Cond .
0.06
7.3 350
7.6 325
7.6 400
7.6 400
0.05 7.4 463
0.01
0.21
0.01
0.06
NA
0.01 7.8 621
0.04
0.06 365
0.09 7.1 300
0.04 6.8 430
Fecal .
Coll.
2
0
2
0
0
5
148
0
3
0
7
0
3
26
2
0
(continued)
-------
TABLE 17. (Continued)
Ul
Jj L JLllg 11
N02
<0.1
<0.1
<0.1
<0.2
<0.1
<0.1
<.0.1
<0.1
<0.1
< 0.1
<0.1
0.1
< 0.1
< 0.1
< 0.1
a dilution was
' f. v.oul
NH,
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
0.0
used,
i\-ii)
TKN TOC
0.0 31
1.0
0.4
1.2
0.0 4
0.0 1
0.7 8.0
0.4 2.5
0.6
0.2 5
0.7
0.0
3.3
0.9
0.4
0.6
actual value
BOD
2
4.2
1.8
2.5
2
12
2.4
0.7
1.7
4.4
3.35
2.5
8.0
7.3
1.0
9
is less
f
COD TSS
0.0 4.0
66
0.2
4.1
1,400 4.0
380
84
6.8
9.2
12
3.7
10
280
1.8
4.7
than 10,000
Total
P0a PH
0.09
7.3
7.6
7.6
7.6
0.05 7.4
0.03
0.20
0.07
0.39
NA
0.01 7.8
0.00
0.10
0.04 7.0
0.05 7.0
Spec.
Cond.
350
325
400
400
463
682
340
300
420
Fecal.
Coli.
2
0
2
0
0
13
391
0
oa
29
0
0
0
10
43
0
(Continued)
-------
TABLE 17. (Continued)
Location: Well #1
Date
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
a Bottle
NO 3 N02
9.1 <0.1
2.2 <0.1
3.4 <0.1
4.0 <0.1
4.1 <0.1
4.7 <0.1
0.1 <0.1
0.0
0.3 <0.1
2.0 0.1
0.0 <0.1
0.1 <0.1
froze and broke
NH3
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
TKN TOG
0.9 9.5
0.0 0
0.9 6.0
0.2 4.5
0.6
0.3 8
1.4
1.3
3.7
1.8
0.8
0.6
in transit, may be
BODS
10
25
2.5
0.3
2.5
4.8
6.25
5.8
6.7
7.3
1.7
4.2
subject to
COD TSS
1,400 240
220
36
12
1.8
13
680
41
260
570
65
1.8
contamination
Total
• POu pH
0.17 7.2
0.07
0.38
0.04
0.07
0.08
0.11 7.7
0.02
0.08
0.13 7.6
0.01 7.2
Spec. Fecal.
Cond. Coli.
462 0
22
3
0
8
oa
4
930 0
8
305 0
280 s 0
340 0
(continued)
-------
TABLE 17. (continued)
Location: Well #2
Date
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4*12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
NOs
9.6
0.0
0.0
4.5
0.1
0.3
0.8.
0.0
0.3
0.4
0.0
0.0
N02
<0
<0
<0
<0
<0
0
<0
<0
<0
<0
<0
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
.1
NH3
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.9
3.2
0.0
4.8
TKN
0.0
0.0
0.6
0.4
0.4
1.9
3.7
1.5
5.1
6.4
2.1
6.4
TOG BOD 5
6.5 45
0 135
22 36
13.5 3.
5.
2 4.
6.
6.
4.
4.
4.
3.
2
8
2
7
7
9
3
1
9
COD TSS
1,300 760
240
100
26
23
120
180
65
810
810
4.5
52
Total Spec.
POtj pH Cond .
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
96 7.1 565
05
13
04
01
02
02 7.2 1,840
01
26 1,000
13 7.0 550
01 7.0 610
Fecal.
Coli.
0
<2
0
1
0
0
0
0
0
0
3
0
(continued)
-------
Location: Well #3
TABLE 17. (continued)
oo
Date
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
NO 3
0.2
15
2.1
3.9
4.1
4.9
0.1
0.0
0.4
0.3
0.0
0.1
N02 NH3
<0.1 0.0
<0.1 0.0
0.1 0.0
0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.0
TKN
0.9
0.7
0.7
0.2
0.2
0.0
1.8
0.9
7.0
2.8
0.6
0.7
TOC BOD 5
32 62.5
0 45
4 3.5
1.3 0
1.5
0 2.8
7.45
9.8
8.4
3.6
3.5
5.1
COD TSS
1,700 224
180
39
4.7
0.3
8.0
1,100
25
140
480
3.0
6.5
Total Spec.
POit pH Cond.
0.39 7.0 643
0.03
0.08
0.03
0.01
0.00
0.01
0.03 7.7 796
0.02
0.10 330
0.07 7.2 300
0.01 7.4 450
Fecal.
Coli.
0
5
0
0
0
1
0
0
0
0
0
0
(continued)
-------
TABLE 17. (continued)
Location: Well #4
Date
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
NO, NO,
0.0 <0.1
0.1 <0.1
0.0 <0.1
4.6 <0.1
0.0 <0.1
0.1 <0.1
0.0 <0.1
0.1
0.6 <0.1
0.2 <0.1
0.0 <0.1
0.1 <0.1
NH3
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.2
0.0
0.0
0.0
TKN
0.9
0.0
0.7
0.4
0.6
1.7
3.2
1.5
5.1
3.7
2.3
1.7
TOG BOD,;
98 225
0 120
12.5 8.5
3.0 0.5
7.1
16 2.4
2.5
6.3
6.5
a
2.7
4.0
COD TSS
1,400 276
160
74
8.7
24
56
1,300
68
1,000
1,300
1,745
46
Total Spec.
POU pH Cond .
0.72 6.9 802
0.04
0.08
0.03
0.01
0.08
0.10
0.01 7.3 1,880
0.01
0.19 1,100
0.13 6.8 785
0.26 7.0 800
Fecal.
Coli.
0
<2
0
0
0
0
0
0
0
0
0
0
Lab error
(continued)
-------
Location: Well #5
TABLE 17. (continued)
oo
o
Date
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
Q
No sample,
N03
5.5
3.3
3.4
4.6
3.9
3.3
6.8
4.6
2.1
0.0
bottle
N02 NH3
0.2 0.0
<0.1 0.0
0.1 0.0
0.1 0.0
<0.1 0.0
0.2 0.0
DRY F
<0.1 0.0
<0.1 0.0
<0.1 0.0
TKN
1.8
0.0
0.4
0.6
0.7
2.4
0 R T
0.6
4.0
1.4
0.6
N 0
froze and broke in
TOG BODS
6 24
0 30
3.0 3
2.0 1.0
1.5
10 3.0
HIS SAMP
5.2
2.3
0.6
1.2
SAMPLE
transit
COD TSS
1,200 28
160
36
8.7
10
3.3
LING
5.8
49
1,100
14
Total Spec.
POU pH Cond .
0.11 7.6 281
0.03
0.17
0.04
0.37
0.07
0.05 7.9 503
0.03
0.11 350
0.09 7.1 335
Fecal.
Coli.
55
<2
1
0
0
a
0
0
0
0
(continued)
-------
00
TABLE 17. (continued)
Location: Well #6
Date
6-23-76
9-9-76
10-9-76
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
N03
0.1
0.0
0.0
4.9
1.8
4.2
0.7
N02
0.1
0.1
0.1
O.f
0.1
0.5
0.1
N 0
NH3
0.0
0.0
0.0
0.0
0.0
0.0
0.0
SAM
TKN
3.5
0.0
2.1
0.9
0.4
0.2
0.5
P L E
TOG
11
0
5.5
1.5
7
FROM
BOD5
43
40
14
1.1
1.3
2.3
2.4
HER
COD TSS
1,500 32
160
26
9.1
0
15
9.5
EON DRY
Total Spec.
PO,, pH Cond .
0.07 8.6 261
0.09
0.20
0.06
0.06
0.00
3.56
WELL
Fecal.
Coll.
0
2
0
0
0
0
0
(continued)
-------
Location: Well #7
TABLE 17. (continued)
oo
N)
Date
6-23-76
9-9-76
10-9-77
11-8-76
12-21-76
1-7-77
4-12-77
5-13-77
6-8-77
7-15-77
8-18-77
9-19-77
N03
0.3
0.1
0.6
4.3
1.3
1.0
0.3
5.8
1.9
0.3
0.0
0.0
N02 NH3
0.2 0.0
<0.1 0.0
0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.0
<0.1 0.9
<0.1 0.0
<0.1 0.0
<0.1 0.0
TKN TOC
1.8 5.5
0.0 2
1.0 3.0
0.0 1.0
0.2
0.2 6.0
0.5
0.7
3.7
1.4
1.6
0.6
BOD 5
23
4
0.6
0.9
6
4.1
1.6
1.3
2.4
1.7
5.6
COD TSS
1,500 44
160
32
7.3
0
11
7.8
5.4
41
1,100
13
8.8
Total Spec.
POit pH Cond .
0.10 8.7 141
0.04
0.08
0.05
0.02
0.00
0.022
0.02 7.5 415
0.02
0.04 160
0.04 8.2 135
0.01 7.2 170
Fecal .
Coli.
0
<2
1
0
0
0
0
0
0
0
0
0
-------
TABLE 18. HEAVY METAL DATA FOR FOURTEEN WATER SAMPLING POINTS
Location
Influent
Effluent
Well #1
Well #1
Well #2
Well #2
Well #3
Well #3
Well #4
Well #4
Well #5
Well #5
Well #6
Well #6
Well #7
Well #7
Under drain
Under drain
Spring #2
Spring #2
Spring #1
Spring #1
Flat Creek
Flat Creek
Date Cu*
9-9-76 <0.01
9-9-76 <0.01
6-23-76 <0.01
9-9-76 <0.01
6-23-76 <0.01
9-9-76 <0.01
6-23-76 <0.01
9-9-76 <0.01
6-23-76
9-9-76
6-23-76
9-9-76
6-23-76
9-9-76
6-23-76
9-9-76
6-23-76
9-9-76
6-23-76
9-9-76
6-23-76
9-9-76
6-23-76
9-9-76 <0.01
ZN Cd Pb Ni
<0.01 <0.01 <0.1 <0.1
0.07 <0.01 <0.1 <0.1
0.14 <0.01 <0.1 <0.1
<0.02 <0.01 <0.1 <0.1
0.08 <0.01 <0.1 <0.1
0.04 <0.01 <0.1 <0.1
0.06 <0.01 <0.1 <0.1
<0.02 <0.01 <0.1 <0.1
0.08
0.02
0.05
<0.02
0.06
<0.02
0.05
<0.02
0.04
<0.02
0.02 0.1
<0.02 0.1
0.02 0.1
<0.02 0.1
0.03 0.1
<0.02 <0.01 <0.1 <0.1
* All parameters are measured in mg/1.
83
-------
TABLE 19. CHEMICAL ANALYSIS FOR FOURTEEN WATER SAMPLING POINTS
00
4S
Location
Influent
Effluent
Water tap
men's room
South lagoon
SW corner
Spring above
transit pipe
Transit pipe
from lagoons
Date Para
6-4-75 Sfl
mg.
1
>-15-75 Si
m
i
1C-18-75 =2*
mg.
1
6-4-75 2fL
mg
1
7-7-75 =f
m&
1
6-4-75 2f
as.
i
6-4-75 2f
mg
1
7-7-75 Sf
mg.
1
Ca
3.28
66
3.39
68
5.09
100
2.6
52
3.62
73
2.75
55
3.26
65
3.55
71
Mg
1.63
20
1.68
26
2.10
26
1.6
19
1.84
24
1.51
18
1.60
20
2.50
30
Na
18.92
435
1.47
34
2.51
58
0.05
1.1
0.23
5.4
0.05
1.1
0.19
4.3
0.21
4.8
K
0.36
14
0.51
20
1.55
61
0.01
0.2
0.04
1.6
0.01
0.2
0.05
2.1
0.03
1.2
CO 3
0.0
0.0
0.0
0
0
0
0
0
0
0
0
0
0
0
0
0
HC03
5.93
362
5.5
240
4.05
250
3.42
207
4.25
260
3.63
222
4.39
268
4.75
290
SO,,
0.24
12
0.0
0
0.67
32
0.67
32
0.62
30
0.70
34
0.58
28
0.50
24
C12
17.98
634
1.15
41
1.89
67
0.05
1.8
0.9
32
0.10
3.6
0.21
7.3
1.18
42
NOa
0.10
0.5
0.0
0.3
0.01
0.6
0.01
0.6
0.09
5.5
0.01
0.6
0.01
0.5
0.11
7.0
Total %
Fl C03 tfa Boron Silica
0.07
1.3
0.08
1.5
0.08
1.6
0.01
0.2
0.01
0.2
0.01
0.2
0.01
0.2
0.01
0.2
(continued)
-------
TABLE 19. (continued)
Ui-
Location
North lagoon
HE Corner
Date Para
10-15-76 Sfi
M
1
1-25-76 3f
m&
1
2-21-76 5p
S£
1
7-7-76 SSI
mg
1
Ca
3.99
80
3.14
63
2.91
58
3.29
66
Mg
1.93
24
1.73
21
1.37
17
2.21
27
Na
3.05
70
3.08
71
2.05
47
0.30
7.0
K
1.47
57
0,87
34
0.49
19
0.07
2.8
CO 3
0
0
0
0
0
0
0
0
HC03
3.6
220
0
0
1.60
98
4.65
280
SO,,
0.75
36
0.69
33
0.74
35
0.60
29
C12
1.73
61
—
—
1.23
61
0.72
25
NO 3
0.01
0.5
0.01
0.6
0.01
0.8
0.0
t).l
Fl C03 NA Boron
0.08
1.5
0.18
3.4
0.08
1.5
0.01
140 4 3
0.2
Silica
20
16
11
-------
APPENDIX
II. RESULTS OF CLIMATIC MONITORING
86
-------
TABLE 20. DEPTH TO WATER TABLE IN SPRAYFIELD (METERS)
Date
9-26-75
8-12-76
10-976
11-19-76
12-20-76
1-4-77
5-12-77
6-8-77
8-16-77
9-16-77
Well 1
4.87
3.69
4.73
4.99
4.65
5.29
4.66
4.48
4.65
5.06
Well 2
2.61
3.12
3.86
4.03
4.19
4.28
4.72
3.75
3.96
3.52
Well 3
2.52
3.02
4.19
4.47
4.75
5.85
4.95
4.04
4.24
4.73
Well 4
3.52
4.20
5.65
5.91
6.13
6.25
4.92
5.25
5.43
6.26
Well 5
3.97
3.26
6.31
6.99
7.33
7.45
4.71
5.27
6.06
Dry
Well 6
1.43
1.41
3.06
3.87
4.60
4.97
—
—
—
—
Well 7
3.59
3.76
5.64
6.00
8.17
6.95
5.90
5.62
6.28
7.04
87
-------
TABLE 21. HOURS PER MONTH OF IRRIGATION FOR EACH SECTION OF SPRAYFIELD
Month
December
January
February
March
April
May
June
July
August
September
October
November
December
January
February
March
April
May
June
July
August
September
Year
1975
1976
1976
1976
1976
1976
1976
1976
1976
1976
197.6
1976
1976
1977
1977
1977
1977
1977
1977
1977
1977
1977
Set #2
8
33
80
91
78
59
44
52
56
34
47
67
66
30
72
30
Set #3
8
33
94.5
91
86
44
34
51
56
47
47
63
72
54
96
55
Set #4
105.5
115
74
45
50
56
60
58
52
75
61
64
Operator
42
32
Set #5
98
49
66
60
45
54
54
49
49
50
62
64
sick, no
83
46
Set #6
52
90
78
112.5
147.5
83
319.5
42
93
54
58
45
62
56
50
50
46
54
41
data
51
58
Set #7
52
81
98
126
116.5
229.5
306.5
40
76
16
70
46
44
52
43
57
45
61
60
56
50
Total
# of hrs.
120
171
176
238.5
264
312.5
692
460
515
374
336
264
319
334
281
302
346
376
313
400
271
Note: The average output per hour of operating time was 170 cubic meters.
88
-------
(0.52)
00
15
CJ
o
2 io
3
4J
cd
H
>> 0
9
-5
-10
M
M
J
(0.06)
(0.13)
SONDJFMAMJJASOND
1975 1976 1977
Figure 19. Mean Monthly Temperatures for Thayne, Wyoming. () Empirical probabilities of
observing mean monthly temperatures less than or equal to the specified values.
-------
VO
o
e
o
•H
4J
4J
•H
CX
•H
U
n
>*
o
s_
vO
CM
o
s_
x->
m
m
o
N_
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-600/2-78-139
3. RECIPIENT'S ACCESSION"NO.
4. TITLE AND SUBTITLE
LAND APPLICATION OF WASTEWATER UNDER HIGH ALTITUDE
CONDITIONS
5. REPORT DATE
July 1978 issuing date
6. PERFORMING ORGANIZATION CODE
John Borrelli
Robert D. Burman
Ronald H. Delanev
Joseph L. Moyer
Hugh W. Hough
Barron L. Weand
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
The University of Wyoming
University Station
Post Office Box 3354
Laramie, Wyoming 82071
10. PROGRAM ELEMENT NO.
1BC611
11. CONTRACT/GRANT NO.
R803571
12. SPONSORING AGENCY NAME AND ADDRESS
Robert S. Kerr Environmental Research Laboratory
Office of Research and Development
U.S. Environmental Protection Agency
Ada. Oklahoma 74820
13. TYPE OF REPORT AND PERIOD COVERED
Final - 1975-1978
14. SPONSORING AGENCY CODE
EPA/600/15
15. SUPPLEMENTARY NOTES
16. ABSTRACT
The objectives of this study were to monitor and evaluate the nutrient, crop, and
hydrologic parameters affecting the Thayne, Wyoming, wastewater treatment system.
Cheeseplant wastewater and municipal sewage were mixed, pretreated, and applied to
a 15 hectare sprayfield on a year-round basis. An ice pack formed during November
or December, depending on weather conditions, and lasted through the middle of April.
Samples of groundwater and water from adjacent springs have shown that after three
consecutive years (1975-77) of spraying wastewater on the field and with a build-up
of the ice pack each winter, no significant amounts of pollutants have reached the
groundwater. Organic nitrogen was oxidized as it traveled through the ice pack and
upper part of the soil mantle during the winter. Reduction of BOD^, COD, and
nitrogen forms to migrate in the ice pack was observed, clearly showing the concen-
tration of these parameters at the surface and bottom of the ice pack. Garrison
creeping foxtail appeared to be most adapted to the sprayfield of those species
tested. Reed canarygrass, smooth bromegrass, and western wheatgrass were also able
to survive the harsh environment of the sprayfield. The forages studied could, at
specific stages of growth, contain sufficient N03~N to be toxic to livestock.
17.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.lDENTIFIERS/OPEN ENDED TERMS
c. COSATI Field/Group
Land use/
Sewage treatment/water reclamation
Environmental engineering/waste disposal/
Water quality/
Soil water/ Ground water/
Land treatment/
sewage effluents
Land pollution abatement
Land management/
environmental management
High altitude spray
irrigation
68D
68C
48G
48B
48E
13. DISTRIBUTION STATEMENT
RELEASE TO PUBLIC
19. SECURITY CLASS (ThisReport)
UNCLASSIFIED
21. NO. OF PAGES
100
20. SECURITY CLASS (Thispage)
UNCLASSIFIED
22. PRICE
EPA Form 2220-1 (9-73)
92
« u.s. ommiafr nmne offlK: 1971—7 57.140 /1377
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