EPA-660/2-75-013
JUNE 1975
Environmental Protection Technology Series
Treatment and Ultimate Disposal of
Cattle Feed lot Wastes
National Environmental Research Center
Office of Research and Development
U.S. Environmental Protection Agency
Corvallis, Oregon 97330
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development,
U.S. Environmental Protection Agency, have been grouped into
five series. These five broad categories were established to
facilitate further development and application of environmental
technology. Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface
in related fields. The five series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioecononric Environmental Studies
This report has been assigned to the ENVIRONMENTAL PROTECTION
TECHNOLOGY STUDIES series. This series describes research performed
to develop and demonstrate instrumentation, equipment and methodology
to repair or prevent environmental degradation from point and
non-point sources of pollution. This work provides the new or
improved technology required for the control and treatment of
pollution sources to meet environmental quality standards.
EPA REVIEW NOTICE
This report has been reviewed by the Office of Research and
Development, U.S. Environmental Protection Agency, and approved
for publication. Approval does not signify that the contents
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products constitute endorsement or recommendation for use.
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EPA-660/2-75-013
JUNE 1975
TREATMENT AND ULTIMATE DISPOSAL OF
CATTLE FEEDLOT WASTES
By
Harry L. Manges
Ralph I. Lipper
Larry S. Murphy
William L. Powers
Lawrence A. Schmid
Kansas State University
Manhattan, Kansas 66506
Grant No. S800923
ROAP/Task No. 21BEQ/011
Program Element 1BB039
Project Officer
David M. Farmer
Robert S. Kerr Environmental Research Laboratory
National Environmental Research Center
P. 0. Box 1198
Ada, Oklahoma 74820
NATIONAL ENVIRONMENTAL RESEARCH CENTER
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
CORVALLIS, OREGON 97330
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ABSTRACT
A study was conducted to determine the characteristics of beef feed-
lot wastes, both runoff and manure, and the optimum application rate
of these wastes to land. The project was located at a commercial
beef feedlot in southcentral Kansas.
Characteristics of beef feedlot wastes varied widely with season.
Near maximum corn forage yields, without excessive accumulation of
salt in the soil, were obtained from waste application rates neces-
sary to meet nitrogen fertilizer recommendations. At these waste
application rates, basic intake rate of water into the soil was in-
creased. Net income from irrigated corn production was sufficient
to make application of feedlot manure with disposal as the main ob-
jective unprofitable.
Land application rates of beef feedlot wastes should be based upon
the results of laboratory analyses of wastes from each feedlot.
Feedlot wastes should be applied at rates necessary to meet nitrogen
fertilizer recommendations. A salt-alkali test should be made
annually on the surface soil to monitor changes in soil salinity
levels.
This report was submitted in fulfillment of Grant Number S800923,
by Kansas State University under the partial sponsorship of the
Environmental Protection Agency. Work was completed as of December,
1973.
ii
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CONTENTS
Page
Abstract ii
List of Figures v
List of Tables ix
Acknowledgements xi
Sections
I Conclusions 1
II Recommendations 3
III Introduction 5
IV Project Facilities 12
V Runoff Characterization 14
VI Manure Characterization 23
VII Effect of Anaerobic Lagoon Storage on 27
Runoff Quality
VIII Feedlot Runoff Disposal onto Land 30
IX Manure Disposal onto Land 48
X Micronutrient Relationships to Land Disposal 71
of Feedlot Wastes
XI Denitrification Study 91
XII Runoff from Land Application of Feedlot Wastes 107
111
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Sections
XIII Movement of Water into Soil Receiving 115
Feedlot Manure
XIV Economics of Waste Application to Land 120
T ?fi
XV References
XVI Publications 133
XVII Glossary of Abbreviations and Symbols 135
iv
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No.
FIGURES
Influence of Season on COD 15 cm Below the 28
Surface of Lagoon 119
Electrical Conductivity of Saturated Paste 35
Extracts from Surface (0-15 cm) Soil Samples
as Affected by Accumulative Applications of
Beef Feedlot Lagoon Water
Nitrate-Nitrogen Content of Soil Cores as 36
Affected by Depth and Average Yearly Application
Rate of Beef Feedlot Lagoon Water
Bray P-l Extractable P Content of Soil Cores 37
as Affected by Depth and Average Yearly Appli-
cation Rate of Beef Feedlot Lagoon Water
Extractable K Content of Soil Cores as Affected 38
by Depth and Average Yearly Application Rate
of Beef Feedlot Lagoon Water
Extractable Na Content of Soil Cores as Affected 39
by Depth and Average Yearly Application Rate of
Beef Feedlot Lagoon Water
Electrical Conductivity of Saturated Paste 41
Extracts from Soil Cores as Affected by Depth
and Average Yearly Application Rate of Beef
Feedlot Lagoon Water
Corn Forage Yield (Metric Tons/Hectare, 42
Corrected to 30% Dry Matter) as Affected by
Accumulative Applications of Beef Feedlot
Lagoon Water
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FIGURES (Continued)
9 Uptake of N by Corn Forage as Affected by 44
Accumulative Applications of Beef Feedlot
Lagoon Water
10 Uptake of P by Com Forage as Affected by 45
Accumulative Applications of Beef Feedlot
Lagoon Water
11 Uptake of K by Corn Forage as Affected by 46
Accumulative Applications of Beef Feedlot
Lagoon Water
12 Nitrate-N Content (Dry Weight Basis) of Corn 47
Forage as Affected by Accumulative Applications
of Beef Feedlot Lagoon Water
13 Electrical Conductivity of Saturated Paste 50
Extracts from Surface (0 to 15 cm) Soil Samples
as Affected by Accumulative Applications of
Beef Feedlot Manure (Dry Weights) that Began
in 1969
14 Nitrate-N Content of Soil Cores as Affected by 54
Depth and Average Accumulative Applications
of Beef Feedlot Manure (Dry Weights) that Began
in 1969
15 Ammonium-N Content of Soil Cores as Affected by 55
Depth and Average Accumulative Applications of
Beef Feedlot Manure (Dry Weights) that Began
in 1969
16 Extractable Na and K of Soil Cores as Affected 56
by Depth and Average Accumulative Applications
of Beef Feedlot Manure (Dry Weights) that Began
in 1969
17 Extractable P of Soil Cores as Affected by Depth 57
and Average Accumulative Applications of Beef
Feedlot Manure (Dry Weights) that Began in 1969
18 Corn Plant Populations as Affected by Accumu- 59
lative Applications of Beef Feedlot Manure
(Dry Weights) that Began in 1969
19 Corn Forage Yields (Corrected to 30% Dry Matter) 60
as Affected by Accumulative Applications of
Beef Feedlot Manure (Dry Weights) that Began
in 1969
vi
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FIGURES (Continued)
No. Page
20 Uptake of N and P by Corn Forage as Affected 62
by Accumulative Applications of Beef Feedlot
Manure (Dry Weights) that Began in 1969
21 Nitrate-N Content of Corn Forage (Dry Weight 63
Basis) as Affected by Accumulative Applications
of Beef Feedlot Manure (Dry Weights) that Began
in 1969
22 Electrical Conductivity of Water Saturated Paste 64
Extracts from Surface (0 to 15 cm) Soil Samples
as Affected by a Single Application of Beef
Feedlot Manure (Dry Weights) in 1969
23 Extractable Na and K Content of Soil Cores as 67
Affected by Depth and a Single Application of
Beef Feedlot Manure (Dry Weights) in 1969
24 Nitrate-N and Extractable P Content of Soil 68
Cores as Affected by a Single Application of
Beef Feedlot Manure (Dry Weights) in 1969
25 Corn Forage Yield (Corrected to 30% Dry Matter) 70
Four Years After a Single Application of Beef
Feedlot Manure (Dry Weights) in 1969
26 DTPA Extractable Fe as Affected by Depth and 74
Applications of Beef Feedlot Wastes
27 DTPA Extractable Zn as Affected by Depth and 81
Applications of Beef Feedlot Wastes
28 Zinc Concentrations in Corn Leaf Tissue and 82
Corn Forage as Affected by Accumulative Yearly
Applications of Beef Feedlot Manure (Dry
Weights) that Began in 1969
29 DTPA Extractable Mn as Affected by Depth and 84
Applications of Beef Feedlot Wastes
30 Manganese Concentrations in Corn Leaf Tissue 85
and Corn Forage as Affected by Accumulative
Yearly Applications of Beef Feedlot Manure
(Dry Weights) that Began in 1969
31 Manganese Concentrations in Corn Forage as 86
Affected by Accumulative Yearly Applications of
Beef Feedlot Lagoon Water that Began in 1970
32 Corn Forage Yield and Manganese Uptake as 87
Affected by Accumulative Yearly Applications of
Beef Feedlot Manure (Dry Weights) that Began in
1969
vii
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FIGURES (Continued)
No.
33 Corn Forage Yield and Manganese Uptake as 88
Affected by Accumulative Yearly Applications
of Beef Feedlot Lagoon Water that Began in 1970
34 DTPA Extractable Cu as Affected by Depth and 90
Applications of Beef Feedlot Wastes
35 Soil-Atmosphere-Access Tube Design 92
36 Total N (Dry Weight Basis) in Soil Cores as 95
Affected by Depth and Two Years of Beef
Feedlot Manure Applications
37 Organic C (Dry Weight Basis) in Soil Cores 97
as Affected by Depth and Yearly Beef Feedlot
Manure Applications
38 Nitrogen Gas in Soil Atmosphere as Affected by 98
Depth and Yearly Beef Feedlot Manure Applica-
tions
39 Oxygen Gas in Soil Atmosphere as Affected by 99
Depth and Yearly Beef Feedlot Manure Applica-
tions
40 Carbon Dioxide in Soil Atmosphere as Affected 100
by Depth and Yearly Beef Feedlot Manure Appli-
cations
41 Nitrous Oxide and Methane in Soil Atmosphere 101
as Affected by Depth and Yearly Beef Feedlot
Manure Applications
42 Nitrate-N, Nitrite-N, and Ammonium-N (Dry 103
Weight Basis) in Soil Cores as Affected by
Depth and Yearly Beef Feedlot Manure Applications
43 Nitrate-N, Nitrite-N, and Anmonium-N in Soil 104
Solution as Affected by Depth and Yearly Appli-
cation of Beef Feedlot Manure
44 Iron and Manganese in Soil Solution as 105
Affected by Depth and Yearly Applications
of Beef Feedlot Manure
viii
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TABLES
No. Page
1 Pratt Precipitation 13
2 Rainfall and Runoff Data 16
3 Characteristics of Rainfall Runoff 18
4 Effects of Pen Cleanliness Upon Runoff 20
5 Characteristics of Snowmelt Runoff , 21
6 Characteristics of Manure Removed from Pens and 24
History Since Previous Cleaning
7 Manure Quality from Pens and Stockpile 25
8 Elemental Composition and Electrical Conductivity 32
of Beef Feedlot Lagoon Water
9 Elemental Composition and Electrical Conductivity 33
of Beef Feedlot Runoff Lagoon Samples Taken at
12 Locations in Kansas During July, 1970 and 1971
10 Corn Forage Yield, Electrical Conductivity of 43
Soil Saturation Extracts (EC), and Uptake by
Corn of Indicated Elements
11 Analysis of Beef Feedlot Manure Applied to 51
Disposal Plots
12 Corn Forage Yield, Uptake by Corn of Indicated 52
Elements, Corn Plant Population, Nitrate-N Content
of Corn Forage, and Electrical Conductivity of Surface
Soil Saturation Extracts as Affected by Accumulative
Yearly Applications of Beef Feedlot Manure (Dry
MT/ha.) that Began in the Fall of 1969
ix
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TABLES (Continued)
No. Page
13 Corn Forage Yield, Uptake of Indicated Elements, 65
Corn Plant Population, Nitrate-N Content of Corn
Forage, and Electrical Conductivity of Surface Soil
Saturation Extracts as Affected by a Single Applica-
tion of Beef Feedlot Manure (Dry MT/ha.) in the Fall
of 1969
14 Average Analysis of Beef Feedlot Manure and Lagoon 72
Water Applied to Disposal Plots
15 The pH (1:1 Soil to Water Ratio) of Selected Soil 72
Cores
16 Corn Forage Yield, Composition and Uptake of 75
Indicated Elements and Corn Leaf Tissue Composition
as Affected by Accumulative Yearly Applications of
Beef Feedlot Manure (Dry MT/ha.) that Began in the
Fall of 1969
17 Corn Forage Yield, Composition and Uptake of 77
Indicated Elements and Corn Leaf Tissue Composition
as Affected by a Single Application of Beef Feedlot
Manure (Dry MT/ha.) in the Fall of 1969
18 Corn Forage Yield, Composition and Uptake of 79
Indicated Elements as Affected by Accumulative
Yearly Applications of Beef Feedlot Lagoon Water
(cm) that Began in the Summer of 1970
19 Nitrogen Balance Calculations in Plots that Had 94
Received Applications of Beef Feedlot Manure
(Dry MT/ha.)
20 Annual Manure Applications to Disposal Plots 108
21 Characteristics of Rainfall Runoff 109
22 Characteristics of Rainfall Runoff 110
23 Mean COD:Pollution Parameter Ratio 111
24 Characteristics of Irrigation Runoff 113
25 Characteristics of Irrigation Runoff 114
26 Manure Application Rate and Basic Intake Rate 116
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ACKNOWLEDGEMENTS
Many people contributed to this project and their help was sincerely
appreciated. Mr. Eugene Goering, Mr. Dean Eisenhauer, and Mr.
Robert Stritzke directed the field operations at the Pratt Feedlot.
Mr. George Wallingford supervised collection of many soil cores at
Pratt and their analyses in the laboratory. Several research assis-
tants, graduate research assistants, and temporary employees helped
with the installation of instruments at Pratt, the collection of
field data, the taking of many soil and plant samples, the applica-
tion of feedlot wastes to the disposal plots, the measurement of
corn forage yields, and the analyses of soil and plant samples in
the laboratory.
The cooperation of those associated with the Pratt Feedlot, Inc.,
is gratefully acknowledged. Special thanks go to Mr. Gary Dodson
who patiently scheduled the project's activities into the day to
day operation of the waste handling and farming systems.
XI
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SECTION I
CONCLUSIONS
The Soil Conservation Service runoff equation predicted volume of beef
feedlot runoff with sufficient accuracy for the design of runoff hand-
ling, storage, and treatment facilities. Concentration of pollutants in
feedlot runoff from rainfall varied widely during an individual runoff
event and from successive runoff events. Concentration of pollutants
in feedlot runoff from snowmelt was about double that in runoff from
rainfall.
Quantity of manure and accompanying soil removed during cleaning of
feedlot pens was quite variable being as low as one kilogram per animal
per day following periods of high biological activity and as high as ten
kilograms per animal per day following prolonged wet periods. In gen-
eral, concentration of volatile solids, nitrogen, and phosphorus in-
creased as quantity of manure removed per animal per day decreased.
Manure collected from a concrete surface had about twice the moisture
content of that collected from a dirt surface, along with a higher
concentration of volatile solids, nitrogen, and phosphorus. There was
no appreciable change in the characteristics of manure during storage
in an undisturbed, compacted stockpile.
Storage of feedlot runoff resulted in apparent chemical oxygen demand
removal of about 65 percent. Even with this removal, the liquid was
far from a quality suitable for direct discharge to a watercourse.
At the end of four years, maximum corn forage yields were obtained from
annual feedlot runoff applications of 29 centimeters. Electrical con-
ductivity of extracts from saturated pastes of surface soil increased
linearily with application rates of feedlot runoff. Significant quanti-
ties of nitrate-nitrogen accumulated in soil receiving annual feedlot
runoff applications of 22 centimeters and greater.
Annual feedlot manure application rates of 29 to 68 dry metric tons per
hectare gave near maximum corn forage yields without excessive accumu-
lation of salt in the soil. Positive effects on corn forage yields
remained four years after a one-time application of up to 450 dry metric
tons per hectare of feedlot manure. In some cases, concentrations of
nitrate-nitrogen in corn forage grown on land receiving more than 40
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dry metric tons per hectare per year of feedlot manure reached levels
at which toxicity can occur if the forage is ingested by animals.
Applications of feedlot wastes did not appreciably change the pH of the
neutral to alkaline soil studied. Soil availability of iron, zinc, and
manganese, as measured by Diethylene Triaraine Penta Acetic Acid extract-
ion, was increased by applications of feedlot runoff and feedlot manure.
Corn forage concentrations of zinc and manganese were enhanced by year-
ly applications of feedlot manure while only the concentrations of
manganese were enhanced by yearly applications of feedlot runoff.
Nitrogen balance calculations for plots receiving yearly applications
of feedlot manure showed large amounts of nitrogen were not accountable
by soil, plant, and manure analyses. Atmospheric and other soil analy-
ses suggested that nitrogen loss occured from denitrification reactions.
In general, concentrations of chemical oxygen demand, nitrogen, and
phosphorus in runoff water from land receiving annual applications of
beef feedlot manure increased with increasing feedlot manure application
rates and were higher from rainfall runoff than from irrigation runoff.
However, five day biochemical oxygen demand was consistently below 10
milligrams per liter in irrigation and rainfall runoff indicating the
soil had assimilated the load applied in the manure.
After four annual applications of feedlot manure, the basic intake rate of
water into the soil increased as manure application rates increased up
to 269 metric tons dry manure per hectare per year and decreased as
annual manure application rates continued to increase.
Annual applications of feedlot runoff at rates sufficient for maximum
irrigated corn forage yields were the most profitable. Net income from
irrigated corn production was sufficient to make application of feedlot
manure with disposal as the main objective unprofitable. Although
annual applications of feedlot manure increased irrigated corn forage
yields, the net return was not sufficient to pay for applying the
manure. Large, first-year applications with no manure added in the four
subsequent years appeared to be profitable.
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SECTION II
RECOMMENDATIONS
Feedlot waste treatment and ultimate disposal can be accomplished by
land application with minimal pollution of the environment. The
following recommendations are based upon the results of this study.
TREATMENT AND ULTIMATE DISPOSAL OF WASTES
As characteristics of feedlot wastes vary widely, land application
rates should be based upon laboratory analyses of wastes from individ-
ual feedlots.
Apply feedlot runoff at a rate which will meet the nitrogen fertilizer
recommendations for the area. Determine area of land needed for feed-
lot runoff disposal by the Soil Conservation Service runoff equation
using historical rainfall records.
The first year feedlot manure is applied to land, apply at twice the
rate necessary to meet nitrogen fertilizer recommendations. Apply at
the rate needed to meet nitrogen requirements in subsequent years.
Single applications of manure sufficient to meet nitrogen requirements
for up to four years may be made with no manure applied in the inter-
vening years.
Collect soil samples annually from the surface six inches and the root
zone of the crop and have them analyzed for salt-alkali and nitrate-
nitrogen, respectively. If the salinity or nitrate-nitrogen level
becomes excessive, adjustments must be made in feedlot waste applica-
tion rates.
Analyze forages grown on soils following the application of greater
than 30 metric tons per hectare of manure for nitrate-nitrogen to
insure they will not be toxic to animal health.
RESEARCH NEEDS
Long-term studies are needed to determine the effects of feedlot waste
application rates to land on characteristics of the soil, percolating
soil water, surface runoff water, and crops grown. These studies
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should be conducted on different soil types and under the range of cli-
matic conditions found in the cattle feeding areas.
Obviously, long-term studies cannot be completed in time to provide
inputs into the planning and construction of feedlot waste disposal
systems started in the near future. The objective of the above recom-
mendation can be met by monitoring changes which occur under the best
designed feedlot waste management systems and effecting changes in the
system's operation as needed to provide for a viable waste treatment
and disposal program.
A large, first-year application of feedlot manure followed by no manure
in the subsequent three years gave most profitable corn forage yields
in this study. Studies are needed comparing annual manure applications
with a large first year application followed by smaller annual applica-
tions and large applications at varying time intervals. Selection of
the optimum waste application rate should be based upon economics and
the potential for pollution of the environment.
Additional research is needed to determine the effects of feedlot
waste application rates and tillage practices on the quality of runoff
waters from irrigation and precipitation.
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SECTION III
INTRODUCTION
BACKGROUND
The trend in the beef industry is towards feeding cattle in large
capacity feedlots. As animals are concentrated in a small area, the
problem of disposing of their wastes is magnified.
Wastes from beef feedlots are in two forms, liquid and solid. Liquids
are the result of stormwater runoff from the feedlot surface. The
solids consist of manure and accompanying soil removed from the pens
during cleaning.
Land disposal of animal wastes may lead to pollution of land, of storm-
water runoff from the disposal site, and of the underlying ground water.
The long-term effects of land disposal of material containing small
amounts of toxic metals such as are in animal wastes has not been
evaluated (Gatehouse1). Neither has the potential for pollution of
runoff from land used for the disposal of animal wastes been measured.
Large concentrations of nitrate-nitrogen, apparently from animal sources,
have been detected in the soils and shallow aquifers underlying some
farmstead areas of northern Missouri (Smith2). These same problems
may occur on land used for disposal of feedlot wastes.
Pollution Potential
Miner ^t al.3 found that feedlot runoff is a concentrated organic waste
high in nitrogenous compounds. High concentrations of total coliforms,
fecal coliforms, and fecal streptococci were measured. Smith and Miner
reported four severe pollution incidents resulting in extensive fish
kills below commercial feedlots in Kansas. Septic conditions, high
biochemical oxygen demand (BOD) and ammonia concentrations, and high
bacterial counts were recorded at the time of observed fish kills
which was immediately following runoff-producing rainfall.
Large volumes of manure are generated in cattle feedlots. According
to the review of literature prepared by Loehrf a 408 kilogram (kg)
steer will generate 4.08 kg of dry manure per day. Manure presents
no serious water pollution threat until it is washed away or removed
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in cleaning operations. The water pollution problem is associated
with disposal of the manure.
Treatment
There are several ways to dispose of feedlot wastes without pollution.
All the techniques fall into one or a combination of three categories;
i.e., chemical, biological, and physical. Chemical treatments appear
to offer less promise than the others for the present due to their
high costs. Controlled biological processes suffer due to the inter-
mittent nature of runoff which comes only with precipitation. Biologi-
cal treatment systems function best when the waste loading rate is
uniform and continuous. Continuous flow of waste could be accomplished
only with flow equalization ponds which would add to the expense of the
waste handling system. Within the area of physical treatment is any
technique which involves primarily manipulation of the waste with ulti-
mate disposal as the goal. Almost without exception, any method for
handling feedlot waste will require ultimate disposal of the residue.
Loehr5 concluded that, at present, there is no profitable method of
livestock manure utilization and it is unlikely that one will be de-
veloped. As a result, the feedlot industry must accept the method of
waste disposal that will prevent pollution at the least cost. The
physical treatment technique appears to be the least expensive for com-
plete disposal of feedlot wastes. Therefore, emphasis in this study is
on the detention of runoff in storage lagoons with disposal of the
runoff and manure onto agricultural land.
Land Disposal
Land disposal was the earliest organized method of waste treatment
(Schraufnagel6). Sewage from the city of Berlin, Germany, was being
applied to 56,000 acres in 1934 (Weise7). According to Schraufnagel,6
sewage farming was still being practiced in 1962 by some large cities
including Paris, Berlin, and Melbourne. Gray8 reported successful
irrigation with effluent from the sewage treatment plant at Lubbock,
Texas. In general, irrigation with sewage effluent has increased crop
yields (Henry £t al.9 Henkelekian,10 Day et al.11).
Liquid manure disposal onto land is now being accepted by certain farm
operators (Wolf,12 McKee13). Care must be taken so that the soil used
as the disposal medium doesn't become polluted. Characterization of
feedlot runoff has shown it to vary widely in chemical composition and,
generally, to be high in total salt content (Miner et al.,1 Clark and
Stewart1^ Gilbertson et^ al.,16 McCalla est al.,17 Satterwhite and Gil-
bertson/8 Swanson e£ auL.17). After runoff arrives at a lagoon, evapo-
ration can further increase salt concentrations. When such lagoon water
is applied to a soil, some of the salts can be used as plant nutrients
to increase productivity but excess salts can create soil salinity and
dispersion problems.
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Only limited data are available on effects of beef feedlot lagoon
water on soil properties and plant growth. Travis et al. found
total salts increased by 200% and infiltration declined to zero in
soil columns from four Kansas soils after inundation with lagoon
water with an electrical conductivity (EC) of 13.4 millimhos per
centimeter (mmhos/cm). They suggested that the higher proportion
of monovalent cations Na+, K+, and KBf in such soil could have dispersed
colloids and led to the cessation of infiltration.
Satterwhite and Gilbertson18 found in a one-year field study that sprink-
ler applications of up to 30.5 centimeter (cm) of lagoon water increased
soil N, P, K, S, and Cl. They compared (in a greenhouse) the effects
of tap water, water taken from a lagoon in 1969, and water from the
same lagoon in 1970 on plant growth. Both lagoon waters increased total
salts in the soil more than did tap water. Growth of nine grass species
was enhanced by tap water and by the 1970 lagoon water, but was inhi-
bited by the 1969 lagoon water.
The ultimate fate of most of the solid wastes produced in beef feedlofs
is application to land. The plant nutrient content of this material is
variable, but usually contains on a dry weight basis 1.0% to 3.54 N,
0.32% to 0.85% P, and 0.75% to 2.35% K (Mathers and Stewart," Mathers
et al.22 Reddell23). Competition for this waste as chemical fertilizer
"suppleinent or replacement is expected to increase but high transporta-
tion costs will still restrict its distribution. When determining land
disposal rates, care must be taken to insure unimpaired productivity of
the soil, optimal utilization of plant nutrients, and minimal loss of
waste components to ground and surface waters. Little agronomic research
has dealt specifically with land disposal of beef feedlot manure at the
high disposal rates being used on fields close to large feedlots.
Herron and Erhart24 found that beef feedlot manure increased yields of
sorghum forage at application rates of 17.5 and 35.0 dry metric tons per
hectare (MT/ha.) on an irrigated calcareous soil compared to plots that
received no treatment and that residual effects on yields were Present
four years after the single manure applications. Approximately 70/o of
the N contained in the manure had become plant available in four years.
Workers in Texas have conducted several studies on the agronomic aspects
of land disposal of beef feedlot manure. Mathers and Stewart (in the
laboratory) mixed manure (3.25% N and 32% C) with a silty clay loamsoil
at six rates of from 0% to 20% manure. From 45% to 52% of the added C
was evolved as C02-C, and from 46% to 50% of the added N was converted
to NH.-N NHt-N and NOo-N during 90 days of incubation. Total mineral-
ization was thus similar for both N and C. Work with similar manure-
soil mixtures in a greenhouse experiment showed that after two croppings,
the value of 2.4 kg of N from manure was equivalent to 1.0 kg of N from
ammonium nitrate for the nutritional requirements of grain sorghum,
expressed as yield. Mathers et al.22 found in a three-year field study
that feedlot manure applications of 269 and 538 metric tons per hectare
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per year (MT/ha./yr) lowered grain sorghum yields and greater than 112
MT/ha./yr reduced corn forage yields. The yield depressions were
attributed to salt buildup in soil. No grain sorghum yield differences
were found between manure application rates of 22.4, 67.3 or 135 MT/ha./
yr. Nitrate-N accumulated in the surface 2 meters (m) of soils receiv-
ing 112 and 224 MT/ha./yr and was increased in sorghum plants to levels
not considered toxic at manure rates of from 22.4 to 269 MT/ha./yr.
Surface soil organic matter and soluble salts were increased by disposal
rates of from 22.4 to 269 MT/ha./yr. Reddell and coworkers23*25
at three locations applied beef manure in single applications of 673,
1350, and 2020 wet MT/ha. (49%, 52%, and 36% dry matter at the three
locations) to soil and covered the manure by deep plowing (91 cm deep).
Yields of corn and sorghum forage for two years after manure applica-
tions were made increased over the control plot (no treatment), with
maximum yields occuring at the 673 MT/ha. rate. The NOf-N content of
both forages was increased to potentially toxic levels at one location
during one of the two growing seasons. At one location, eight treat-
ments of 22.4 to 2020 wet MT/ha. (64% dry matter) were applied and
yields of corn forage and sorghum grain were measured. Maximum corn
forage yields were realized at the 22.4 wet MT/ha. rate and steadily
decreased at the higher rates. Grain sorghum yields increased to the
336 wet MT/ha. rate and decreased relative to the maximum at higher
rates. The depressed growth was again attributed to salt injury.
Micronutrient Relationships
Numerous researchers have found manure to be a source of N (Bunting26
Gamer27 Haworth28 Lindsay?9 Ridley and Hedlin30), P (Bunting26
Garnerf7 Haworth28 Ridley and Hedlin30 Abbott and Lingle31 Carlson
et_ al.*2 Widdowson and Penny33), and K (Bunting26 Garner27 Haworth28
Widdowson and Penny33 Austin3"* Garner35 Haworth36) for improved soil
fertility as reflected in increased crop yields, while others (Bunting26
Haworth28 Austin31* Bishop et al.37 Haworth38 Holliday et al.39)
have reported increased yields that couldn't be traced to improved
availability of N, P, or K. These unexplained yield increases could be
due to improved soil structure (Bunting, Austin31* Haworth39 Holliday
£t al.39 Haworth1*,0 Salter and Haworth1*,1 »'*2»'*3 Williams and Cooke'*4)
and subsequent positive effects on permeability, waterholding capacity,
and soil aeration, or to trace elements contained in the manure. The
trace element content of manure and feedlot runoff is variable (McCalla
eit al. \7 Mathers et al.22 Atkinson et al.1*5 Hensler et al.1|6»i*7).
Manure has increased or not affected soil pH (Bishop ^t_ _al, |7 Hensler
^tal.1*,7 Atkinson .et al. "J8 Barnes et al. I9 Brage £t al. 5(5 Thompson51)
which indicates that altered soil pH may be a mechanism by which manure
can change the availability of soil nutrients.
A deficiency of Fe in corn grown on a soil deficient in Fe and Zn was
partially corrected by applications of poultry manure in a greenhouse
study conducted by Miller et _al.f2 while in the same study, a deficiency
-------
of Zn was completely corrected. Carlson _e_t jal. ^2 found manure to
be a source of Zn in corn grown on a subsoil deficient ii Zn, while
Meeler and Randhawa53 found manure to depress corn yieldu and the uptake
of Zn. Hensler et^ al.1*6*1*7 in a greenhouse study, found that dairy
manure increased corn tissue concentrations of Zn and Fe on unlimed soil
and of Zn and Cu on limed soil, while lowering the Mn concentrations of
corn on the unlimed soil. Increased soil pH was suggested as the reason
for the depressed Mn content. Recovery from the manure of Fe, Zn, Mn,
and Cu generally decreased with increasing manure applications, probably
due to relatively lessoned yield responses. Increased soil pH was also
suggested by Atkinson et_ a]L 't8 as the reason for decreased Mn content of
ladino clover that had received farmyard manure. Depressed Mn content
and unaltered Fe, Zn, and Cu content of vegetable leaves was found by
Page51* Cow manure increased the exchangeable Cu content of a soil in
an incubation study by Guptaf5
Denitrification
The fate of the N fraction of animal wastes after land application has
both economic and environmental importance. If the waste is being used
as a substitute for chemical fertilizers, then emphasis should be on
maximum utilization of the added N by the crop being grown. If land
applications are to provide a means of waste disposal, then there should
be concern about potential contamination of groundwater by N which is
frequently applied in excess of that removed by the crop. Loss to the
atmosphere of nitrogenous gases through denitrification reactions in
soil is a mechanism that lowers the amount of plant-available N and, at
the same time, decreases the potential for groundwater contamination.
Recognition of these facts has prompted scientists to investigate fac-
tors affecting denitrification in soil after waste applications and to
measure the resultant N losses.
Broadbent and Clark56 have reviewed the conditions necessary for or
conducive to denitrification in soil: reducing or anaerobic conditions,
source of easily oxidizable C, basic pH, presence of nitrate-N, relatively
high temperature, and a denitrifying microbial population. Applications
of animal wastes to soil help to promote several of these conditions.
The waste organic matter fraction provides a C source, and stimulated
microbial respiration of this organic matter helps create anaerobic
conditions by removing 02 from the soil atmosphere. Irrigation can
further reduce 02 levels by restricting gas exchange with the above-
ground atmosphere. Mineralization of organic N into NO^-N provides the
denitrification substrate, and some wastes have been shown to increase
soil pH (Hensler et al.^7).
Several researchers have measured N losses in soil after animal waste
applications. Olsen et_ a^. ^7 found in a greenhouse study that 20% to
76% of the N added to soil by dairy cattle manure was lost through
volatilization. Koelliker and Miner58 reported an unaccountable N loss
of 2,307 kilogramsper hectare (kg/ha.) in soil treated with anaerobic
-------
livestock lagoon effluent by a sprinkler system. This loss was attrib-
uted to denitrification.
In a greenhouse study, Mathers and Stewart21 found that N losses appar-
ently due to denitrification were maximized by small, frequent applica-
tions of beef feedlot manure. Larsen and Axley59 calculated that up to
831 kg/ha, of N was being lost by denitrification in soil that had
received sprinkler applications of poultry processing wastes, and Erick-
son et_ al.k° removed 98.8% and 95.8% of the N in liquid swine and dairy
waste, respectively, when applied by sprinkler to a layered soil renova-
tion system. Adriano ^t al.°l estimated that 50% of the excess N added
to soils by dairy cattle wastes is either denitrified or becomes a part
of the organic N pool.
Water Infiltration
Most manure generated in beef feedlots is applied to cultivated land.
Application of manure will alter the soil's composition and thereby
change its water intake characteristics.
Cross and Fischbach62 conducted a two-year study with maximum manure
applications of 582 and 414 metric tons dry matter per hectare the first
and second year, respectively, to a Sharpsburg silt loam soil. They
reported that the initial intake rate increased as manure application
rate increased, the basic intake rate increased with elapsed time from
date of application, basic water intake rate decreased as manure appli-
cation rate increased, and depth of plowing did not appreciably affect
basic intake rate. Swader and Stewart"3 found that three annual appli-
cations of manure at 22, 45 and 112 metric tons per hectare tended to
increase the intake rate into the plow layer of a Pullman clay loam
soil.
SCOPE
Manure generated in beef feedlots and stormwater runoff are sources of
pollution to streams, groundwater, and land. We have postulated that
pollution can be minimized by the orderly disposal of feedlot wastes
onto cropland. This project was conducted to determine the quantity and
properties of wastes generated at a beef feedlot and the optimum waste
application rates onto land with a minimum of pollution to land, its
stormwater runoff, and the groundwater. Of particular concern was the
fate of the large amounts of nitrogen carried in these wastes.
OBJECTIVES
The objectives of the project were:
a. To characterize stormwater runoff from the feedlot area.
b. To characterize manure generated in the feedlot.
c. To determine the effect of storage in an anaerobic lagoon
on the quality of feedlot runoff.
10
-------
To determine the influence of different feedlot runoff
loadings on the soil, the soil leachate, stonnwater
runoff from the treated soil, and corn yields.
To determine the influence of different manure loadings on
the soil, the soil leachate, stormwater runoff from the
manured soil, removal of nutrient elements from the soil
by corn, and corn yields.
To determine the most economical loading of feedlot
runoff and manure onto land compatible with pollution
control.
11
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SECTION IV
PROJECT FACILITIES
GENERAL
This project was conducted at the Pratt Feedlot, Inc., a 33,000-head
commercial beef feedlot located 10 kilometers (km) north of Pratt,
Kansas. The feedlot was built on an abandoned World War II air base.
Feedlot Pens
Driveways for delivering feed to feedbunks built along both their sides
are located in the center of the concrete runways. Feedlot pens extend
away from the feedbunks with access alleys for handling cattle at their
lower end. The surface of the pens slopes away from the feedbunks with
runoff water carried across the access alleys into drainage channels.
The upper 20% to 25% of the pen area is on the side of the concrete
runway and the remaining pen area has a dirt surface.
Waste Handling Facilities
Stormwater runoff from the feedlot is directed into storage reservoirs.
A sewage pump has been installed in each reservoir. The sewage pumps
are interconnected with an underground plastic pipeline which is also
connected to an irrigation well. Feedlot runoff and well water can be
pumped onto approximately 80 hectares (ha.) of land which has been
leveled for surface irrigation. Two tailwater recovery pits are located
at the lower end of the irrigated fields to return runoff from irriga-
tion to the storage reservoirs. The waste disposal system has been
approved by the Kansas State Department of Health and is licensed as
required by Kansas law.
Manure is removed from the feedlot pens after the cattle are sold and
before a new group arrives. The manure is windrowed with a motor gra-
der. A paddle scraper then loads the windrowed manure and carries it to
a stockpile where it is stored until land is open for disposal. Manure
is spread onto cultivated land in the spring before the soil is tilled
or in the fall after crops are harvested.
12
-------
Waste Disposal Plots
Sixty plots were established in 1969 for waste disposal studies. The
plots were located approximately 0.8 km from the feedlot pens. Twenty
plots, 4 treatments and a control replicated 4 times in a randomized
block design, received applications of feedlot runoff. All plots were
9.1 meters (m) wide and contained 12 rows of corn. Two replications
were on an odd shaped area of land with plot lengths varying from 60 m
to 110 m. The plots in the other 2 replications were 64 m long.
Manure was applied to 40 plots, 9 treatments and a control replicated 4
times in a randomized block design. All plots were 9.1 m wide and 64 m
long and contained 12 rows of corn.
The predominant soil on the waste disposal study area has been classi-
fied as Farnum loam with 2 replications of the runoff disposal plots
extending onto Naron fine sandy loam (USDA - Soil Conservation Ser-
vice6^). As the original land surface was undulating, considerable
areas of subsoil were exposed during leveling for surface irrigation.
Laboratory analyses show the surface soil to be a silty clay loam with a
cation exchange capacity of 19 milliequivalents (meq) per 100 grams (g)
and a pH of 7.0.
Precipitation
The Pratt Feedlot, Inc., is located in Southcentral Kansas where pre-
cipitation is quite variable. Table 1 gives monthly precipitation for
the period 1969 through 1973 along with monthly normals measured at the
National Weather Service station 3 km east of Pratt.
Table 1. PRATT PRECIPITATION4
Month
January
February
March
April
May
June
July
August
September
October
November
December
Annual
1969
cm
T
4.67
5.71
4.14
11.00
7.16
9.22
16.46
15.93
5.59
0.08
1.42
81.38
1970
cm
0.89
0.28
6.73
6.88
9.68
3.73
2.64
3.35
8.61
5.38
T
0.23
48.40
Year
1971
cm
1.78
5.79
0.51
3.65
6.73
14.07
9.52
0.97
3.71
14.00
6.65
1.17
68.46
1972
cm
0.63
T
0.42
2.90
13.41
9.47
17.83
9.78
5.41
2.34
7.72
4.27
74.19
1973
cm
4.29
3.05
22.02
8.18
1.37
1.19
15.01
2.44
24.03
13.49
1.32
7.49
103.88
Normal
cm
1.45
2.74
3.56
5.13
8.66
9.73
7.34
7.26
6.43
5.74
2.16
2.29
62.49
National Weather Service station 3 km east of Pratt.
13
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SECTION V
RUNOFF CHARACTERIZATION
GENERAL
The volume of feedlot runoff from individual rainfall events must be
known for proper sizing of storage reservoirs. Characteristics of the
runoff will influence its optimum application rate to cropland. Rainfall-
runoff relationships and characteristics of feedlot runoff were determined.
METHODS AND PROCEDURES
Runoff was characterized from two separate areas of the Pratt Feedlot,
Inc., which were designated Area 119 and Area 2.
Area 119 consisted of one feedlot pen, 75 m deep and 93 m wide, along
with adjacent access areas and covered 0.82 ha. Approximately 18 m
across the upper end of the pen adjacent to the feedbunks were surfaced
with concrete; the remaining area had a dirt surface. Drainage was
diagonally across the pen on about a 1% slope into an anaerobic lagoon.
Runoff from Area 119 was directed through a 0.4572-meter H-flume equipped
with a water level recorder and an automatic vacuum sampler. A float
device rose in response to flow to activate the water level recorder and
sampler. Sampling was controlled by a time clock with a sample drawn
every 10 minutes for up to the first four hours of a runoff event.
Area 2 consisted of 25 feedlot pens covering 11.1 ha. Total drainage
area was 13.3 ha. including pens, drainage channel to the flow measuring
and sampling station, and access areas. All lots were 92 m deep with
widths varying from 40 m to 61 m. Approximately 18 m across the upper
end of the pens adjacent to the feedbunks were surfaced with concrete;
the remaining area had a dirt surface. Lots were mounded along the
sides to provide a dry area for the cattle during wet weather. Mounds
were 1.2 m above the drainage path which ran down the center of each
pen. Lot drainage slopes were 1.3%. Runoff from the individual pens
was collected in a drainage ditch with a slope of 0.26 percent and
conveyed to a storage reservoir.
14
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Runoff from Area 2 was directed through a 0.762-meter Parshall flume
equipped with a water level recorder and an automatic vacuum sampler.
Flow was measured and sampled by the same procedure as for Area 119.
Runoff samples were collected from the samplers and refrigerated soon
after a runoff event. The samples were packed in ice and transported to
Manhattan, Kansas, where they were again refrigerated until laboratory
analyses were made. Runoff samples were analyzed for chemical oxygen
demand (COD) by acid oxidation according to Standard Methods55 for
total N by the micro-kj eldahl method, for total P by acid digestion
followed with colorimetric procedures, for total solids (TS) by evapo-
ration, for volatile solids (VS) by combustion, for NH^-N and NO^-N
by steam distillation procedures, for EC by a resistance meter, and for
Ca, Mg, Na, and K by standard atomic absorption and flame photometric
procedures.
Precipitation was measured with a recording rain and snow gauge located
adjacent to Area 119. As Area 2 was about 1 km from Area 119, rainfall
was also measured with 3 non-recording rain gauges evenly distributed
across Area 2.
RESULTS AND DISCUSSION
Volume of Runoff
Depth of rainfall and resulting runoff from individual rainfall events
are given in Table 2 for Areas 119 and 2. As the Soil Conservation
Service (SCS) runoff equation is used in the design of soil and water
conservation structures, its application to feedlots was evaluated.
The SCS runoff equation (SCS National Engineering Handbook66) is:
(P - 0.51 S)2 (1)
** P + 2.03 S
where Q = Surface runoff, cm
P = Rainfall, cm
S = Potential maximum retention of water
(interception by vegetation, surface storage, and
infiltration into the soil) , cm
S is evaluated from the equation:
10 (2,
where CN = Runoff curve number
15
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Table 2. RAINFALL AND RUNOFF DATA
Rainfall
cm
Runoff
cm
5-day
antecedent
moisture
cm
Runoff
curve
number
Area 119
1.84
0.81
1.93
1.30
0.51
,22
,24
0.38
,63
,19
Mean
0.31
0.02
0.71
0.73
0.18
0.07
1.47
0.01
0.73
0.25
0.00
1.83
2.65
0.13
1.42
0.00
0.00
2.24
0.00
0.00
Area 2
88
90
93
97
98
88
97
95
95
93
93
1,93
1.78
2.79
0.38
1.35
4.06
1.24
3.56
0.30
Mean
0.30
0.40
1.48
0.00
0.23
1.66
0.29
2.22
0.09
—
2.65
2.11
0.00
2.24
0.00
0.00
0.00
1.19
4.37
—
87
91
94
94
91
88
93
94
99
92
The runoff curve number for each runoff event was determined by substi-
tuting measured rainfall and runoff into Equations 1 and 2. Table 2
gives calculated runoff curve numbers. Mean runoff curve numbers were
93 for Area 119 whose surface was one-fourth concrete and three-fourths
dirt with an area of 0.82 ha. and 92 for Area 2 whose surface was one-
fifth concrete and four-fifths dirt with an area of 13.3 ha. The
slightly lower runoff curve number and lower volume of runoff from Area
2 can be attributed to increased infiltration in the longer drainageways
from the larger drainage area.
Miner et^ al.llf reported runoff curve numbers of 91 and 94 for feedlot
surfaces of dirt and concrete, respectively. From their work, the
weighted runoff curve number for Areas 119 and 2 is 92, which was the
mean calculated for Area 2.
16
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Antecedent moisture condition (rainfall during the preceding five days)
is normally considered when predicting runoff by the SCS method. Aver-
age moisture conditions were assumed for the above analysis. A plot of
predicted runoff using mean runoff curve numbers versus measured runoff
indicated a low degree of correlation, but the scatter of points indi-
cated the errors were random. Table 2 gives antecedent moisture condi-
tions for each runoff event. When antecedent moisture conditions were
considered, a plot of predicted runoff using mean runoff curve numbers
indicated a higher degree of correlation, but runoff was consistently
underpredicted and the errors were not random. These results on the
effects of considering antecedent moisture conditions when evaluating
runoff curve numbers are in agreement with the SCS National Engineering
Handbook.66
The influence of antecedent moisture conditions on runoff from a feedlot
surface is difficult to correlate with antecdent moisture conditions for
cropland or grassland because:
a. In addition to rainfall, there is water from daily animal
excretion.
b. Movement of the animals continually stirs the surface and
evaporation is increased.
c. Infiltration into the manure pack of a dry feedlot surface
(low antecedent moisture condition) is high due to its
high organic matter content.
d. Infiltration into the manure pack under average and high
antecedent moisture conditions is very low.
e. Movement of water through the manure pack to the underlying
soil is minimal.
f. Surface storage is high under average antecedent moisture
conditions, due to the many indentations formed by the
hoofs of the cattle.
Based upon the data collected and the above considerations, we have
concluded that runoff curve numbers of 91 and 94 for feedlot surfaces of
dirt and concrete, respectively, are appropriate for both low and aver-
age antecedent moisture conditions. For high antecedent moisture con-
ditions, runoff curve numbers of 97 and 98 are applicable for dirt and
concrete surfaces, respectively. Where runoff flows directly off a
small feedlot into an adjacent storage reservoir, runoff curve numbers
of 92 and 95 are appropriate for dirt and concrete surfaces, respective-
ly for low and average antecedent moisture conditions and a runoff
curve number of 98 is applicable for all surfaces for high antecedent
moisture conditions.
Quality of Rainfall Runoff
Table 3 gives the range, mean, and standard deviation of measured
pollutional parameters for rainfall runoff for Areas 119 and 2. Con-
centration of pollutional parameters varied widely during individual
runoff events and between runoff events as evidenced by the large
17
-------
Table 3. ' CHARACTERISTICS OF RAINFALL RUNOFF
Parameter
COD
N
P
TS
VS
VS
mi. M
« Qji, ll
NOa - N
Na
K
Ca
Mg
EC
Units
mg/£
mg/£
mg/£
mg/£
%
mg/£
mg/£ -
ag/*
mg/£
mg/£
mg/Jl
mg/£
nnnhos/cm
Range
Area
16,100-861
1,580-165
242-9
19,252-214
60-12
9,552-36
580-0
48-0
2,970-31
2,990-29
402-31
183-35
15-1
Mean
119
7,596
675
79
8,442
45
3,888
159
10
560
796
181
98
7
Standard
deviation
3,255
364
42
5,190
12
2,680
112
18
551
586
83
29
3
Number
of
observation
72
55
56
48
48
48
81
81
81
81
81
81
78
Area 2
COD
N
P
TS
VS
VS
NH* - N
NOa - N
Na
K
Ca
Mg
EC
mg/£
mg/£
mg/Jl
mg/Jl
%
mg/Jl
mg/£
mg/A
mg/Jl
mg/£
mg/£
mg/£
mmhos/cm
14,309-1,514
962-85
482-19
17,669-2,971
70-38
11,437-1,429
285-14
45-0
735-67
2,150-134
1,040-40
228-22
11-1
6,111
494
87
7,528
51
3,891
141
5
334
851
187
86
5
2,631
211
89
2,622
7
1,627
57
6
132
480
124
40
2
85
51
86
63
63
63
99
99
99
99
99
99
99
18
-------
standard deviations from the means. There was no significant difference
in quality of runoff from the two areas.
Concentration of pollutional parameters decreased as the runoff hydro-
graph was rising and increased as it was falling. This trend can be
attributed to increasing solubility of material on the feedlot surface
as rainfall continues. When rainfall ends and runoff subsides, the
liquid flowing off is that water which was in contact with the manure
pack and, consequently, of highest pollutant concentration. No correla-
tion was found between pollutant concentrations and runoff rate because
of the variability of runoff quality with time, as well as runoff rate
during a runoff event and differences in pollutant concentrations from
successive storms.
COD of rainfall runoff, expressed in milligrams per liter (mg/O, was
found to be correlated with climatological parameters rather than flow
rate as follows:
COD = 65,313 + 18.37 t - 428 M,. - 1,033 Tg + A.387 W,.; r = 0.79 (3)
where COD = Chemical oxygen demand, mg/il
t = Time since runoff began, minutes
M5 = 5 day antecedent moisture, cm
T = Mean daily ground temperature, °C
g
W = Total wind travel for 5 days prior to the runoff event,
5 km
r = Correlation coefficient
Ground temperature data were taken from a depth of 10.2 cm at the
Hutchinson Experimental Field, 41 miles to the northeast and wind data
were taken from Kanopolis Dam, 78 miles to the northeast of Pratt.
These were the closest stations where soil temperatures and wind travel
were recorded.
Approximately 40% of the variation in COD concentration could be at-
tributed to changes in ground temperature, with COD varying inversely
with temperature. This was expected as biological activity about
doubles with each increase in temperature of 10° C. With warm ground
temperatures much of the organic material, as indicated by COD values,
will be stabilized on the feedlot surface and not be carried away by
subsequent runoff.
N, P, TS, and VS concentrations in mg/S, were correlated with COD by the
following relationships:
N = 0.091 COD - 137; r = 0.88 (4)
P = 0.036 COD - 153; r = 0.64 (5)
19
-------
TS = 2.74 COD - 11,120; r - 0.52 (6)
VS = 1.08 COD - 2,132; r - 0.84 (7)
N and VS were highly correlated with COD as should be expected because
all three parameters are indirectly a measure of organic strength.
Although statistically significant at the 0.01 level, P and TS were not
so highly correlated with COD.
Natural occurrences in 1970 allowed for evaluation of the effects of. pen
cleanliness upon runoff. Pen 119, which was the watershed for Area 119,
was cleaned on June 8 and stocked with cattle on June 10. Rainfall of
about 1.3 cm fell 11 days prior to cleaning of the pen and 3 days after
pen cleaning. Table 4 gives concentration of pollutional parameters
and total quantity of runoff. The only significant differences in
quality were in concentrations of TS and VS. Total solids were higher,
statistically significant at the 0.05 level, in runoff from the cleaned
pen because of the higher volume of runoff due to reduced surface
storage. Volatile solids were higher, statistically significant at the
0.001 level, in runoff from the uncleaned pen because of the larger
amount of organic matter present.
Table 4. EFFECTS OF PEN CLEANLINESS UPON RUNOFF
Condition
Before Cleaning
After Cleaning
Total
runoff
m3
58.8
74.1
Mean Concentrations
COD
mg/S,
5,665
4,315
N
mg/X.
364
396
P
mg/J,
71
52
TS
mg/fc
7,904
10,895
VS
%
53
27
Quality of Snowmelt Runoff
Table 5 gives the range, mean, and standard deviation of measured pol-
lutional parameters for snowmelt runoff from Areas 119 and 2. Concen-
trations of pollutants were about double those measured from rainfall
runoff.
Solids Accumulation Within a Runoff Storage Lagoon
In September of 1971 following a dry summer, the liquid from the lagoon
below Area 119 evaporated, leaving the solids behind. A topographic map
of the lagoon had been prepared following its construction. The area
was resurveyed in order to determine the net accumulation of solids.
The material remaining could best be described as having the appearance
20
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Table 5. CHARACTERISTICS OF SNOWMELT RUNOFF
Parameter
COD
N
P
TS
VS
VS
NH^ - N
N03 - N
Na
K
Ca
Mg
EC
COD
N
P
TS
VS
VS
Units
mg/£
mg/£
mg/£
mg/fc
%
mg/£
mg/A
mg/£
mg/£
mg/£
mg/Jt
mg/4
ramhos/cm
mg/A
mg/8,
mg/Jl
mg/i.
%
mg/£
Range
Area 119
21,700-11,520
1,860-1,080
270-122
21,530-10,744
63-61
13,628-6,586
1,370-446
30-10
1,130-369
3,300-1,080
666-202
222-79
22-9
Area 2
35,764-7,299
2,337-590
459-65
36,684-9,282
65-50
23,551-5,253
Mean
16,060
1,450
171
15,097
62
9,460
674
18
584
1,699
350
122
12
13,767
1,033
209
19,308
57
11,620
Standard
Deviation
3,566
379
55
4,679
1
3,026
247
6
208
561
129
44
4
8,087
617
171
11,425
6
7,924
Number
of
Observations
9
6
6
6
6
6
16
16
16
16
16
16
15
23
8
12
10
10
10
-------
of swamp mud. It was nearly odorless and appeared to be well stabi-
lized. Samples were taken and combined in order to arrive at an average
characteristic for this material.
The volume of accumulated solids was 143 m? The characteristics were
as follows: moisture (dry basis) - 73%, VS - 19.1%, total N - 0.093%,
and total P - 0.094%. As solids had accumulated for two years from the
0.8-ha. area and stocking rate was 250 head, solids accumulation was
0.29 m3 per year per head of feedlot capacity. This figure will be
highly variable depending upon feedlot slope, soil conditions, manage-
ment practices, and length and gradient of the channel carrying runoff
from the feedlot pens to the storage lagoon as well as frequency, quanti-
ty, and intensity of precipitation.
22
-------
SECTION VI
MANURE CHARACTERIZATION
GENERAL
Large quantities of manure are generated in beef feedlots. Land area
required for disposal depends on quantity of manure and its character-
istics. When the feedlot pens were cleaned, the quantity and character-
istics of the manure were determined.
METHODS AND PROCEDURES
Usually, feedlot pens are cleaned prior to the arrival of each new group
of cattle. During cleaning operations, 5% to 20% of the loads selected
at random were weighed and grab samples taken for laboratory analyses.
The manure samples were analyzed for N and P by steam distillation and
colormetric procedures after a sulfuric acid digestion, for VS by com-
bustion, and for moisture content by drying at 105° C for 48 hours.
RESULTS AND DISCUSSION
Table 6 gives quantity and quality of dry manure removed during cleaning
operations along with a history of the pens since they were last cleaned.
Quantity of dry manure removed during cleaning varied from 1.18 to 10.25
kg per animal per day depending on the season of the year. The smaller
quantity removed during July, August, and September reflects losses due
to biological action and wind and water erosion during the feeding
period while the larger quantities with a lower percentage of VS removed
during the remainder of the year reflect increased dirt content when the
feedlot surface remained damp to wet. Comparison of the quantities of
manure removed on July 27 and 28, 1970, shows that larger animals
defecate larger quantities.
The upper 18 m of the pen, adjacent to the feedbunks, was paved with
concrete. The remainder of the pen had a dirt surface. Table 7 pre-
sents some results of manure samples collected from the dirt portion of
the lot and the concrete portion at two different times of the year,
July and November. The manure from the concrete portion had a much
higher moisture content, more than double that of the dirt portion.
This can be attributed to the lack of drainage and to more defecation
23
-------
Table 6. CHARACTERISTICS OF MANURE REMOVED FROM PENS AND HISTORY SINCE PREVIOUS CLEANING
N>
-O
Date
Cleaned
08/21/69a
10/07/69a
11/14/69
01/12/70
02/16/70
02/25/70
03/27/70
06/08/70
07/27/70
07/28/70
09/21/70
11/11/70
12/02/70
12/22/70
05/06/71
05/07/71
05/18/71
Pen size
width
m
45. 7
91.4
45.7
45.7
45.7
45.7
45.7
91.4
45.7
45.7
61.0
91.4
30.5
45.7
91.4
91.4
91.7
depth
m
91.7
74.4
91.7
91.7
74.4
74.4
74.4
74.4
74.4
74.4
76.2
74.4
74.4
74.4
74.4
74.4
45.7
Cattle data
per weight
pen, in,
# kg
188
152
297
298
209
173
147
143
126
251
134
119
223
299
96
124
288
259
176
254
320
267
291
291
278
348
284
336
316
305
371
299
304
335
318
324
341
305
weight feeding
out, period,
kg days
479
477
399
500
493
485
534
495
536
490
519
544
503
509
537
523
507
530
528
153
137
140
147
153
155
141
163
129
138
149
139
146
146
144
147
138
159
160
Per animal day
dry volatile
manure, solids,
kg kg
4.67
5.99
3.54
6.17
6.49
5.40
4.40
4.85
1.72
2.36
1.18
3.99
5.99
6.76
10.25
7.94
7.76
-
-
-
-
-
2.10
-
2.41
0.94
1.00
0.62
1.79
2.05
3.06
2.79
2.29
2.23
Dry manure
N, P,
% %
1.20
1.21
1.08
-
-
-
-
1.96
4.43
3.85
-
2.92
2.83
3.58
0.83
1.57
0.84
0.55
-
-
-
-
-
-
2.34
0.89
0.76
-
0.80
0.66
0.79
0.52
0.52
0.53
Pens not cleaned between groups of cattle.
-------
Table 7. MANURE QUALITY FROM PENS AND STOCKPILE
Date
7/13/70
11/04/70
7/08/70
11/11/70
Fall 1969b
Fall 1970C
Fall 1971°
Sample
location
Dirt
Concrete
Dirt
Concrete
Composite
Top layer
0.3 m deep
0.6m deep
0.9 m deep
1.2m deep
1.5 m deep
—
—
~
Moisture
% of dry wt
10.2
23.4
20.0
47.8
—
46.3
42.7
54.7
52.7
51.8
32.7
Stockpile
—
—
—
Kjeldahl-N
. % of dry wt.
Pen 119
2.00
4.37
2.76
6.10
Stockpile
3.95
3.05
4.00
3.22
3.88
3.71
2.78
Application to Field
1.04
3.12
1.02
Total-P
%of dry wt.
0.50
1.30
0.70
1.47
0.74
0.64
0.80
0.80
0.86
0.71
1.15
Plots
0.39
0.71
0,36
Volatile solids
% of dry wt.
56.2
68.8
35.8
64.8
31.7
31.7
32.9
35.2
3718
33.0
37.3
26.7
42.2
21.1
Stockpile was 1.8 m deep.
kAverage of 28 samples.
cAverage of 24 samples.
-------
because it is at the feeding area. This fresher material at the bunk
also contained more N and P and had a higher VS content, indicating that
it was of higher organic strength. The sample taken from the dirt area
of the lot contained an unknown amount of soil worked into the manure
pack by the hoofs of the cattle.
The manure stockpile was sampled during 1970. These results are pre-
sented in Table 7. Samples were taken while the manure was being
removed from the stockpile in November, 1970, and analyzed in the labo-
ratory. There appeared to be no appreciable difference in manure quali-
ty with depth especially considering the variations that would be ex-
pected from the lots themselves. Also, there was no significant dif-
ference in quality between sampling dates of July 8 and November 11,
1970. It was concluded that manure storage by stockpiling results in no
significant change in quality if the stockpile is not disturbed during
the storage period.
The quality of manure applied to the field disposal plots in the fall of
1969, 1970, and 1971 is presented in Table 7. The N, P, and VS content
of the manure in 1970 was considerably higher than in 1969 and 1971 due
to the lower precipitation during the year. Less dirt was worked into
the manure pack by the hoofs of the cattle during this relatively dry
year. For all three years, the quality of manure applied to the dis-
posal plots was comparable with lot samples taken during the year.
Additional characteristics of manure applied to the disposal plots are
given in Section IX of this report.
26
-------
SECTION VII
EFFECT OF ANAEROBIC LAGOON STORAGE ON RUNOFF QUALITY
GENERAL
As feedlot runoff cannot be discharged to a stream, it must be caught
and stored in a reservoir until it can be treated prior to release or
spread onto land. The natural treatment taking place in an anaerobic
storage lagoon was evaluated.
METHODS AND PROCEDURES
A lagoon was constructed to capture all the runoff from one individual
feedlot pen designated Area 119. The lagoon was 30.5 m x 36.6 m at the
bottom and was 4 m deep. This pond retained all runoff from the area
for runoff events of 1970. The only liquid lost from the pond was by
evaporation or seepage. Samples were collected near the pond center
from a raft. Samples were taken 15 cm below the surface and just above
the bottom and analyzed by the procedures given in Section V of thxs
report.
RESULTS AND DISCUSSION
The values of COD for the sample nearest the surface are plotted in
Figure 1. The surface samples represent that part of the pond which
would be effluent if a discharge were allowed or if it were taken off for
irrigation. The early spring samples from the pond exhibited the
greatest values of COD, N, and P. This was also true of the runoff,
though as mentioned previously, ground temperature has an inverse
effect upon COD. After a period of heavy rains in late May and early
June, the COD in the pond was about 6000 ing/A. There was no significant
runoff again until August 15. Within this period, the COD at the pond
surface was reduced to about 2000 ng/i, or a reduction of about 65%.
During this period, the lagoon contents were being reduced by seepage
and evaporation which would result in a concentrating effect on the
pollutional parameters. The concentrating effect would best be shown
iy what happened to the total solids. Total solids showed a gradual
increase from about 4000 mg/fc in the middle of June to about 7000 mg/i
in the middle of August, with no significant inflow. Taking into
account the concentrating effect, the effective COD removal would be
27
-------
to
00
9000
7000 -
5000
§
CJ
3000 -
1000 -
APR, ' MAY ' JUNE ' JULY ' AUG. ' SEPT, ' OCT. ' NOV. ' DEC,
1970
Figure 1. Influence of season on COD 15 cm below the surface of Lagoon 119-
-------
even higher than that just stated. Total N and P did not show any great
change during this period. The lower-level sample from the pond did not
vary from the upper level sample until August. Samples taken after this
time showed higher COD, N, P, and solids values. The results were
variable, though, as a few cm change in sampling depth near the sludge
zone significantly changed the results.
Solids in the pond bottom were actively decomposing, as indicated by the
bubbling action that occurred. This would also have the effect of
keeping the lagoon contents partially mixed. The odor from the pond was
probably no greater than what might be expected from a feedlot pen
covering the same area.
29
-------
SECTION VIII
FEEDLOT RUNOFF DISPOSAL ONTO LAND
GENERAL
The most common method of disposal has been to apply lagoon water to
adjacent crop and pasture land. High transportation costs dictate that
maximum rates be applied to fields close to the source. The effect of
furrow irrigation with beef feedlot lagoon water on growth and composi-
tion of corn forage and chemical properties of soil was evaluated.
METHODS AND PROCEDURES
Lagoon water was applied by furrow irrigation in increments of 5 cm and
10 cm during the summers of 1970, 1971, 1972, and 1973 to plots 9.1
m wide and 60 to 110 m long. Five treatments were replicated four
times. In 1970 and 1973, the last 10-cm increment of lagoon water was
not applied to the four plots receiving heaviest applications until
after harvest. Inflow and outflow were measured on each plot. The
average amounts applied after four years were calculated to be 0, 7,
13, 22, and 37 centimeters per year (cm/yr) for the four replications.
The two replications that were sampled for soil core analysis had re-
ceived an average of 0, 8, 17, 26, and 45 cm/yr by the fall of 1970; 0,
8, 15, 23, and 43 cm/yr by the fall of 1971; and 0, 7, 14, 20, and 41
cm/yr by the fall of 1972. Samples of the lagoon water were collected
during each application and analyzed for Ca, Mg, Na, and K by standard
atomic absorption and flame photometric procedures, for NH^-N and N03-N
by steam distillation procedures (Keeney and Bremner67), and for soluble
salts by resistance measurements using a Wheatstone bridge.
To compare composition of the material being applied at the study site
with that found at other feedlots, samples were taken from 12 locations
in Kansas during early July of 1970 and 1971 and were analyzed in the
manner described above. The lagoons were sampled at four depths in
1970: 5, 50, 100, and 200 cm. Chemical composition did not vary with
depth in 1970, so a single sample was taken at 15 cm from each lagoon in
1971.
All plots received a preplant irrigation in the spring of 1971 and 1972.
Additional well water was applied during the growing seasons to the
30
-------
control plots and to plots receiving the lower lagoon water treatments
so all plots received approximately equal volumes of liquid. No chemi-
cal fertilizers were applied.
Corn silage yields (mechanical harvest) were recorded, and forage
samples from each plot were analyzed for Ca, Mg, Na, and K by atomic
absorption and flame photometry after a nitric-perchloric acid diges-
tion. N and P were determined by steam distillation and colorimetric
procedures, respectively, after a sulfuric acid digestion. The 1972 and
1973 forage were analyzed for NO^-N by hot-water extraction and sub-
sequent analysis by steam distillation.
Composite surface soil samples (0 to 15 cm) were taken at 18 locations
in each plot after harvest. Extracts from a water-saturated paste were
analyzed for soluble salts by resistance measurements. Cores were taken
after harvest to a depth of 2 m in 1970 and 3 m in 1971 and 1972 from
plots in two replications. The surface meter of each core was divided
into 10-cm increments and analyzed for extractable Ca, Mg, Na, and K by
atomic absorption and flame photometry. For the 1970 and 1971 cores,
the extraction procedure included an initial extraction with methanol to
remove the cations not on exchange sites. This was followed by extrac-
tion with 1.0 N ammonium acetate, pH 7.0, to remove the exchangeable
cations. The 1972 cores were extracted with ammonium acetate only.
Except for Na, only insignificant concentrations were found in the
methanol extract. The total cations extracted by these two methods are
referred to as extractable Ca, Mg, Na, or K. The surface meter incre-
ments also were analyzed for Bray P-l extractable P. The lower depths
were divided into 20-cm increments and, along with the upper depths,
analyzed for NC-3-N by steam distillation techniques (Keeney and
Bremner 67)_ xhe 1972 cores were anoayzed for soluble salts to a
depth of one meter by resistance measurements of extracts from water-
saturated pastes.
RESULTS AND DISCUSSION
Lagoon Water Analyses
Results of analyses of the lagoon water applied are given in Table 8.
Total salt concentration, indicated by the electrical conductivity, was
high. Concentrations of the monovalent cations NH^, iC*", and Na were
considered to be high. The high and low values of all measurements show
how the composition of the lagoons of a single feedlot can vary. This
variation was not accounted for in our interpretation of soil and plant
measurements.
Table 9 includes the analyses of the lagoon samples taken at the 12
Kansas locations. Wide variation in composition of samples among la-
goons each year was similar to variation of lagoon water applied. There
was little correlation between the 1970 and 1971 data from the same
locations. Lack of uniformity between lagoons and between years makes
31
-------
Table 8. ELEMENTAL COMPOSITION AND ELECTRICAL CONDUCTIVITY OF BEEF FEEDLOT LAGOON WATER
High
Low
Average
Electrical ^ Total
conductivity Na K Ca Mg NH^-N NO~-N solids
mmho/cm mg/£
7.6 660 1840 615 239 179 63 18134
1.6 112 259 83 35 41 1879
3.1 295 671 225 87 73 13 4771
COD
6445
593
1868
Volatile
solids
44.4
27.1
37.8
-------
Table 9. ELEMENTAL COMPOSITION AND ELECTRICAL CONDUCTIVITY OF BEEF FEEDLOT RUNOFF
LAGOON SAMPLES TAKEN AT 12 LOCATIONS IN KANSAS DURING JULY, 1970 AND 1971
Location
a
b
c
1
2
3
4
5
6
7
8
9
10
11
12
Lagoon
Electrical
Conductivity
1970b 1971°
nunho /cm
3.1 3.0
2.7 2.7
3.3 4.1
1.0 4.8
4.2 3.9
6.3 4.3
8.6 12.6
12.6 4.2
7.3
a 10.6
— a 1.4
a 6.0
dry at sampling
Na
1970b 1971°
142
139
221
73
268
339
653
1690
834
a
a
a
time.
The 1970 data are averages of
rni* _ 1 n T 1 J_j . rr .. _ _ • _ _ -i
122
220
293
329
335
299
1320
403
a
1460
317
500
samples
K
1970b 1971°
387
166
330
52
550
826
1100
2030
752
a
a
a
taken at
583
325
604
617
729
708
1920
458
a
2210
483
750
depths
Ca
1970b 1971C
ppm
152
101
160
65
141
177
523
403
212
a
a
a
of 5, 50
101
100
158
127
143
135
310
136
a
108
101
187
, 100
Total Inorganic
Mg N
1970b 1971° I970b 1971C
74
61
85
34
97
78
153
189
112
a
a
a
and 200
78
70
111
124
81
89
171
82
a
235
64
170
cm.
195
164
151
16
220
130
366
207
221
a
a
a
145
119
167
161
61
218
543
127
a
136
133
143
The 1971 data are from a single sample taken at a depth of 15 cm.
-------
it essential that analysis of lagoon wastewater be known before disposal
to predict how the material will affect soil properties and plant
growth.
Effects on Soil Chemical Properties
Electrical conductivities of saturation extracts from 1970, 1971, and
1972 surface soil samples were linearly related to the accumulative
depth of lagoon water applied (Figure 2). The EC values of plots re-
ceiving an average of 7 cm/yr were not much higher than those of the
control plots. Plots receiving 13, 22, or 37 cm/yr had EC values
generally higher than the control plots. Since the EC measurement is
directly related to total water-soluble salt content of a soil, the
three heaviest treatments provided more salts than could be used by the
corn plants or leached lower into the profile. High values for the
coefficient of multiple correlation squared (R2) for all three years
(0.878, 0.875, and 0.914) indicate good correlation between the EC
measurement and accumulative amounts of lagoon water applied. This
suggests that EC measurements could be used to estimate amounts of
lagoon water that have been applied to a soil.
To improve the graphical presentation of the soil-core analysis data,
measurements taken from two plots receiving the same treatment were
averaged. Data points were further reduced by combining data from
adjacent depth increments, so that in Figures 3, 4, 5, and 6 values are
plotted for depths of 10, 30, 50 cm, etc., rather than at depths of 5,
15, 25, 35, 45, 55 cm, etc.
Figure 3 gives NO^-N concentrations in the 1970, 1971, and 1972 soil
cores. In 1970, all plots that received lagoon water had higher NO^-N
concentrations at the 10- and 30-cm depths than did control plots. No
NO^-N accumulated deeper than 30 cm in 1970. Soil cores taken in 1971
showed accumulations at 10-, 30-, and 50-cm depths at all disposal
rates. The 23— and 43-cm/yr rates caused particularly high concentrations
at 10- and 30-cm depths. A NO^-N peak was found at 100 cm under the
plots that received 43 cm/yr. In 1971, peaks were less well defined at
200 and 240 cm under the plots that had received lagoon water treatments
of 15 and 43 cm/yr, respectively. By 1972, there was significant move-
ment of NO^-N to the 240-cm depth under plots that had received 20 and
41 cm/yr. Because the control plots received no additional N, their
NCT-N levels were lower than what would be expected in an irrigated soil
being managed for maximum corn production. The two highest disposal
rates were, therefore, the only treatments that caused significant
accumulations of NO~-N in the soil profiles.
J
All disposal rates caused extractable P to accumulate to a depth of 10
cm in the 1970, 1971, and 1972 soil cores (Figure 4). Movement to the
50-cm depth was found under plots receiving 41 cm/yr in 1972. The
general lack of P movement indicates that the capacity of the soil to
immobilize the added P had not been exceeded except possibly at the
highest application rate.
34
-------
1.6
FRLL 1970
o.o-
0 10 20 30 40 50
Accumulative Lagoon Water, CM
FflLL 1972
3.2
.2.4
1.6-
o
0.8
0.0-
-I •—— T-
3.2
FflLL 1971
a:
o
x
O
X
2.U-
1.6-
W
0.8-
0.&
66 88 110
Accumulative Lagoon Water, CM
'0, 3'Q 6'0 90 120 150
Accumulative Lagoon Water, CM
Figure 2. Electrical conductivity of saturated paste extracts from surface (0-15 cm) soil samples
as affected by accumulative applications of beef feedlot lagoon water.
-------
MO-
5 BtH
X
gi2C
FflLL 1970
160-t*
3k
snnJ
300
O—O COMTRDU
«—• 8 CM/TEHR
17 CM/TERR
26 CM/TEHR
8 12
N1TRRTE-M, PPM
FflLL 1972
16
FflLL 1971
CONTROL
7 CIVTEflR
1H CM/TEflR
20 CM/TERR
Ul CM/TEflR
S 16 24 32
NITBflTE-NITROGEN. PPH
9—0 CONTROL
«—. e CM/TERR
15 CM/TERR
23 CH/TEflR
43 CM/TERR
300
I'S 3'0 45
N1TBBTE-N. PPM
Figure 3. Nitrate-nitrogen content of soil cores as affected by depth and average yearly applica-
tion rate of beef feedlot lagoon water.
-------
zo-
5 "0-
3 60-
100
FRJ.L .19,70.
FRLL 19.71
0—O CONTROL
«—» 8 C.VYEHR
a—* 17 CM/YERR
26 CH/YEflfl
US CM/YEflR
9 18 27
PHOSPHORUS, PPM
FfiH 1972
36
0—0 CONTROL
«—» 7 CM/YERR
1U
20
50 ' 75 ' T5o "~ 125
. PPM
20-
60-
ICO
CONTROL
8 CM/YERB
15 CM/TERR
23 CM/TERR
43 CM/TERR
22 44 66
PHOSPHORUS. PPM
88
no
Figure 4. Bray P-l extractable P content of soil cores as affected by depth and average yearly
application rate of beef feedlot lagoon water.
-------
u>
00
20- »—«
80
100
FRLL 1970
c.
bJ
O
00
10
CONTROL
8 CM/TERR
17 CM/ YEflR
28 CH/TERR
«tS CH/ TEflH
CONTROL
7 CM/TEflfi
j« CH/TERR
20 CH/TEflR
Ul CM/TEflfl
ISO 300 "450 600 750
POTRSSIUH. PPM
20-
so-
8t>
0 90 180 270 380 ISO
EXTRBCTflBLE POTBSSIUM. PPM
FflLL 1972
100
19.71
CONTROL
8 CM/TERR
IS CM/TEBR
23 CM/TtRR
IJ3 CK/TERR
200 itOO 600 600
POTRSS1UM. PPH
900
"TblSo
Figure 5. Extractable K content of soil cores as affected by depth and average yearly application
rate of beef feedlot lagoon water.
-------
10
60
80
100
FflLL 1970
CONTROL
8 CM/YEBR
17 CM/TERR
26 CM/TERR
us CM/TERR
120 150 180 210
EXTBBCTB8LE SODIUM, PPM
FRLL 1972
210
CONTROL
7
CM/TEBR
CM/TEBR
CM/TERR
80
120
T5b~
200
20-
5
60-
80-
JOO-
FflLL 1971
CONTROL
8 CH/TEflR
15 CM/TEBR
23 CM/TEBR
43 CM/TEBR
80 120
500IUH, PPK
160
200
Figure 6. Extractable Na content of soil cores as affected by depth and average yearly application
rate of beef feedlot lagoon water.
-------
Analyses of the 1970 coxes for extractable Na, K, Ca, and Mg and analy-
ses of 1971 and 1972 cores for extractable Ca and Mg showed no trends
due to treatment. Extractable K was Increased to a depth of 10 cm in
the 1971 cores and to 30 cm in the 1972 cores at all disposal rates
(Figure 5). Movement below these depths was probably restricted by
exchange reactions with clay colloids. Extractable Na accumulated at
all depths in the 1971 and 1972 cores (Figure 6). Deeper movement of Na
than K reflects greater competitiveness of K for cation exchange sites.
Soluble salts, as indicated by the EC measurements of the 1972 soil
cores, had increased throughout the top meter under plots receiving 14,
20, and 41 cm/yr (Figure 7).
Effect on Yield. Elemental Uptake And NO^-N Content Of Corn Forage
Thirty-five centimeters of lagoon water had been applied to the plots
receiving heaviest treatments by the time the 1970 corn forage was
harvested. There was a general linear trend in yield due to treatment
in 1970 (Figure 8). That positive effect on yield in 1970 probably
resulted from increased soil fertility (nutrients in the lagoon water).
Maximum yields were recorded at the 26-, 22-, and 29-cm/yr rate in 1971,
1972, and 1973, respectively. Yields fell off at higher application
rates, which gave a quadratic relationship between accumulative appli-
cations and yield in 1971, 1972, and 1973 (Figure 8). The initial
increase in yield again can be attributed to improved soil fertility,
while the yield decline at the higher rates likely resulted from salt
buildup in the soil (Figure 2). Yield depression was less in 1973
probably because of higher rainfall that year. The yield decline was
relative; all plots receiving lagoon water yielded more than control
plots.
Uptake of N, P, K, Ca, Mg, and Na was calculated from the yield and
elemental analyses of the corn forage. Linear and quadratic coeffi-
cients and intercepts from a regression analysis on uptake as affected
by the accumulative applications of lagoon water are presented in Table
10. In 1970, uptake of all elements increased linearly with applica-
tions as did the 1970 yield. Uptake in 1971 and 1972 was a quadratic
function of treatment as was yield. Maximum uptake of most elements
occurred at about the same application rate that gave the highest yield
(Figures 8, 9, 10, and 11).
The concentration of NO^-N increased linearly with accumulative treat-
ment in the 1972 and 1973 corn forage (Figure 12). Two of the values
measured were high enough to be considered dangerous to livestock if
ingested.
40
-------
FflLL 1972
o-
20-
40-
31
I—
Q_
60-
80-
100-
(3—m CONTROL
«—e> 7 CM/YERR
x—x m CM/YERR
x—x 20 CM/YERR
x—* 41 CM/YERR
0.0
0.5
1.0 K5 2.0
EC, MMHOS/CM
2.5
Figure 7. Electrical conductivity of saturated paste extracts from
soil cores as affected by depth and averago yearly appli-
cation rate of beef feedlot lagoon water.
Al
-------
FflLL 19.70
90-
TT^tT^" 2'H " 32
Accumulative Lagoon Water, CM
FflLL 1372
60
FPLL 19.71
2"2 1"t 6'6 *8 UO
Accumulative Lagoon Water, CM
FflLL 1973
Figure 8.
JO 6-0 9'0 120 ' ISO "6 • 3'5 ' 70 ' tOS UO 175
Accumulative Lagoon Water, CM Accumulative Lagoon Water, CM
Corn forage yield (metric tons/hectare, corrected to 30% dry matter) as affected by
accumulative applications of beef feedlot lagoon water.
-------
Table 10. CORN FORAGE YIELD , ELECTRICAL CONDUCTIVITY OF SOIL
SATURATION EXTRACTS (EC), AND UPTAKE BY CORN OF INDICATED ELEMENTS
Measurement (y)
Yield (MT/ha.)
N uptake (kg /ha.)
P uptake (kg/ha.)
K uptake (kg/ha.)
Ca uptake (kg/ha.)
Mg uptake (kg/ha.)
Soil EC (mmho/cm)
Yield (MT/ha.)
N uptake (kg /ha.)
P uptake (kg /ha.)
K uptake (kg /ha.)
Ca uptake (kg /ha.)
Mg uptake (kg/ha.)
Na uptake (kg/ha.)
Soil EC (mmho /cm)
Yield (MT/ha.)
N uptake (kg/ha.)
P uptake (kg/ha.)
K uptake (kg/ha.)
Ca uptake (kg/ha. )
Mg uptake (kg/ha.)
Na uptake (kg/ha.)
Soil EC (nmho/cm)
Forage Nitrate-
Nitrogen (ppm)
Yield (MT/ha.)
Forage Nitrate-
Nitrogen (ppm)
3 Data expressed
b Cn crn-i-F-innnt- a*-
R2
0.316
0.482
0.107
0.197
0.0
0.186
0.878
0.372
0.574
0.290
0.079
0.157
0.188
0.387
0.875
0.269
0.584
0.161
0.465
0.212
0.132
0.333
0.914
0.561
0.327
0.482
as factors
t-hp 0.05 1
a
a
1970
0.0
0.0
0.0
0.0
0.0
0.0
1971
-0.004lOb
-0.0221b
-0.00256b
-0.000190
-0.00280
-0.00139 ,
-0.000212
0.0
1972
-0.00322b
-0.0177b
-0.00179
-0.0183b
-0.00237
-0.00117
1972
-0.00106
ba
0.49gb
2.755
0.388
1.60b
0.0890
0.0166
0.425b
2.63\
0.264
0.367
0.301
0.137
0.0261T
0.0191
0.426b
2.91
0.270
2.83b
0.350
0.170
0.00415
0.0200b
5.29b
0.245b
2.26b
a
c
41.5
98.9
33.7
162.0
— — —
19.8
0.495
36.3
85.0
17.2
131.0
20.9
14.8
0.649
0.470
49.2
96.3
29.3
164.0
28.9
21.8
0.558
0.391
-8.86
33.8
75.7
of a regression equation: y =
evel.
F
8.30b
16.75
2.15,
. . , b
4.41
0.0
4.12
129 . 84
5.04J
16.18°
_^D
4.73
1.16
2.07
2.96,
6.39b
125.56°
3.13,
_ o
11.96
1.63,
7.40b
2.28
1.30,
8.99b
190. 87b
23.04b
4.13b
16.76b
2
ax + bx + c
43
-------
POLL 1970
280
'0 7 14 21 28 35
Accumulative Lagoon Water, CM
FflLL 1972
250
so
150
200
1971
"0 22 " «W 66 8'8 liO
Accumulative Lagoon Water, CM
Accumulative Lagoon Water, CM
Figure 9. Uptake of N by corn forage as affected by accumulative applications of beef feedlot
lagoon water.
-------
FRLL 1970
oc
o
*
Ul
X
CT
^f~
-------
300
FRLL 1970
FRLL 1971
100
0 7 I'l 21 2'8
Accumulative Lagoon Water, CM
35
400
FRLL 1972
22 4U 66 88 1
Accumulative Lagoon Water, CM
80-
3'Q 60 9'0 120 " ISO
Accumulative Lagoon Water, CM
Figure 11. Uptake of K by corn forage as affected by accumulative applications of beef feedlot
lagoon water.
-------
1200
z:
Q_
O_
900-
cr
ec
60CH
300-
Accuinulative Lagoon Water, CM
800
s:
n_
Q.
600-
UJ
t—
cc
a:
UOO-
;200-
70 foT 140
Accumulative Lagoon Water, CM
150
175
Figure 12. Nitrate-N content (dry weight basis) of corn forage as
affected by accumulative applications of beef feedlot
lagoon water.
47
-------
SECTION IX
MANURE DISPOSAL ONTO LAND
GENERAL
Application of animal wastes onto land has been used primarily to re-
cover the plant nutrients and to increase crop production. Land appli-
cation as a means of disposal has not been practiced to any large ex-
tent. The effects of a wide range of yearly and residual treatments
of solid beef feedlot manure on the growth of furrow-irrigated corn
forage, on corn forage composition and nutrient uptake, and on the
chemical properties of soil were evaluated.
METHODS AND PROCEDURES
Manure was applied by manure spreaders in the falls of 1969, 1970, 1971,
and 1972 to 24 plots 9.1 m wide and 64 m long (yearly treatments).
Twelve plots received a single manure application in the fall of 1969
(residual treatments). The original experimental design was six yearly
and three residual treatments replicated four times in a randomized,
complete block structure with a control plot in each block that received
no manure or chemical fertilizer. Accurate duplicate measurement of the
large tonnages of manure needed proved impractical. The actual tonnages
applied to each plot were measured by weighing what fell on a 1.858-m2
plastic tarp. Variation from the intended treatments resulted in a
fairly uniform distribution of 114 to 2750 accumulative, dry, MT/ha. of
manure being applied to the plots receiving the yearly treatments after
four years and from 123 to 590 MT/ha. being applied to the residual
treatment plots.
Grab samples were taken from the manure applied to each plot in 1969,
1971, and 1972. The samples were analyzed for Ca, Mg, Na, and K by
atomic absorption and flame photometry after a nitric-perchloric acid
digestion and for N and P by steam distillation and colormetric pro-
cedures after a sulfuric acid digestion.
Corn forage yields (mechanical harvest) were recorded, and samples from
each plot were analyzed in the same manner as the manure samples. In
addition, NO^-N was determined by hot water extraction and subsequent
analysis by steam distillation (Keeney and Bremner67). The corn was
48
-------
furrow irrigated during the summers with approximately 41 cm/yr of well
water and received additional preplant irrigations of approximately 13
cm in 1971 and 1972.
Composite surface soil samples (0-15 cm) were taken at 18 locations in
each plot before preplant irrigation and corn planting in the spring of
1972 and 1973 and again after harvest but before the application of
manure in the fall of 1970, 1971, and 1972. The EC of extracts from
water-saturated pastes of the soil samples was determined by a resis-
tance meter.
Soil cores were taken from each plot in two replications to depths of 1,
1, and 3 m in the spring of 1970, 1971, and 1972, respectively, before
preplant irrigation and corn planting. After harvest but before the
application of manure, soil cores were taken from the same plots to
depths of 2, 3, and 3 m in the fall of 1970, 1971, and 1972, respective-
ly. The surface meter of each core from both samplings in 1970 and 1971
and the fall sampling in 1972 were divided into 10-cm increments and
analyzed for Bray-P-1 extractable P and extractable Ca, Mg, Na, and K.
The cation extraction procedure for the 1970 and 1971 cores included an
initial extraction with methanol to remove cations not on exchange
sites. This was followed by extraction with 1.0 N ammonium acetate, pH
7.0, to remove the exchangeable cations. The fall 1972 cores were
extracted with ammonium acetate only. Except for Na, only insignificant
concentrations were found in the methanol extract. The total cations
extracted by these two methods are referred to as extractable Ca, Mg,
Na, or K. Final measurements for P were made by colormetric procedures,
for Na and K by flame photometry, and for Ca and Mg by atomic absorp-
tion. The lower depths of all cores were divided into 20-cm increments
and, along with the upper depths, analyzed for NO^-N and NH4-N by steam
distillation techniquest (Keeney and Bremner67).
RESULTS AND DISCUSSION
Manure Analysis
The analysis of the manure applied is given in Table 11. The high and
low values show how the manure from a single feedlot can vary. This
variation indicates that analysis of manure should be known before
disposal to predict how the material will affect soil properties and
plant growth.
Effects of Yearly Treatments on Soil Chemical Properties
Electrical conductivities of saturation extracts from surface soil
samples were linearly related to the accumulative MT/ha. of manure
applied at all sampling dates. The highest EC values (Figure 13) were
measured from the spring samplings of 1972 (18.9 mmho/cm) and 1973 (12.0
mmho/cm). In 1973 large increases in EC were measured only in plots
that had received greater than 1200 MT/ha. This means that manure at
49
-------
SPRING 1972
lO'OO ' 1500 " 20'00 2500
RCCUMULRTIVE MflNLIRE RPPLICflTJON, MT/Hfl.
SPRING 1973
J ' 6$0 1200 1800 24*00 ' 3000
flCCUMULflTIVE MftNURE flPPLICflTION, MT/Hfl.
Figure 13. Electrical conductivity of saturated paste extracts from
surface (0 to 15 cm) soil samples as affected by accumu-
lative applications of beef feedlot manure (dry weights)
that began in 1969.
50
-------
Table 11. ANALYSIS OF BEEF FEEDLOT MANURE APPLIED TO DISPOSAL PLOTS
Year H20 N P K Ca Mg Na
percent of dry weights
a
1969 average
1971 average
1972 average
Sample high
Sample low
3-Year average
23.7
13.6
24.3
39.9
4.6
20.5
1.
0.
0.
1.
0.
0.
04
89
84
59
61
92
0.
0.
0.
0.
0.
0.
41
57
57
80
31
52
1.09
0.97
1.37
1.77
0.30
1.14
0.
0.
0.
1.
0.
0.
78
98
99
36
36
92
0.39
0.42
0.42
0.50
0.30
0.41
0.
0.
0.
0.
0.
0.
23
25
29
49
15
26
a
Averages of 36 samples.
Averages of 24 samples.
High and low values are from the 84 samples.
c
those rates provided more salts than could be utilized by the corn
plants or leached lower into the profile. Plots receiving less than
800 MT/ha. by 1973 showed a gradual but not excessive buildup of solu-
ble salts. Since the fall samplings were taken after maximum leaching
of soluble salts by summer irrigations and yearly rainfall, their EC
values were lower than those of the spring sampling of the same year.
The high R2 values found by regression analysis (Table 12) for all
sampling dates indicated that this measurement was highly correlated to
the accumulative MT/ha. of manure applied and that it could be used as
a management tool to monitor the salt status of disposal fields and to
estimate the amount of manure that has been applied to a soil.
To improve the graphical presentation of the soil-core analysis data
from plots receiving yearly treatments, measurements taken from two
plots receiving the same treatment were averaged and the treatments
designated on Figures 14, 15, 16, and 17 by the average accumulative
MT/ha. that had been applied to the two plots up to the sampling date.
Data points were further reduced by combining data from adjacent depth
increments, so that values are plotted for depths of 10, 30, 50 cm,
etc., rather than at depths of 5, 15, 25, 35, 45, 55 cm, etc.
The NOo-N analysis for the spring and fall 1972 cores, both taken after
three years of applications, is given in Figure 14. All but the lowest
51
-------
Table 12. CORN FORAGE YIELD, UPTAKE BY CORN OF INDICATED ELEMENTS,
CORN PLANT POPULATION, NITRATE -N CONTENT OF CORN FORAGE, AND ELECTRICAL
CONDUCTIVITY OF SURFACE SOIL SATURATION EXTRACTS AS AFFECTED BY ACCUMULATIVE
YEARLY APPLICATIONS OF BEEF FEEDLOT MANURE (DRY MT/ha.) THAT BEGAN IN THE FALL OF 1969
Measurement
R
o
N;
1970
Yield (MT/ha.) 0.248 -0.000127b 0.0583b
N uptake (kg/ha.) 0.315 -0.000705:* 0.436b
P uptake (kg/ha.) 0.162 -0.0001097 0.0731b
K uptake (kg/ha.) 0.142 -0.000770 0.418b
Ca uptake (kg/ha.) 0.155 -0.0000956 0.0548
Mg uptake (kg/ha.) 0.164 -0.00845
Population (No./ha.) 0.435 -17.4b
Fall Soil EC (mmho/cm) 0.766 0.00389
45.4
130.0
28.4
191.0
27.7
21.5
48100.0
0.558
8.52
,58
,06
,40
,48?
29.22::
124.56*
Yield (MT/ha.) 0.491
X uptake (kg/ha.) 0.376
P uptake (kg/ha.) 0.297
K uptake (kg/ha.) 0.113
Ca uptake (kg/ha.) 0.247
Mg uptake (kg/ha.) 0.020
Na uptake (kg/ha.) 0.023
Population (No./ha.) 0.418
Fall Soil EC (mmho/cm) 0.782
Forage Nitrate-N (ppm) 0.539
1971
-0.0000446b
-0.000 2 45b
-0.000487
-0.000150
-0.0000298
-0.0000119
-0.00000065
0.00892b
-0.000528b
0.0268
0.214b
0.0427°
0.0123
0.217
0.01162
0.000921
-12.lb
0.00372
0.726b
37.5
123.0
23.6
301.0
22,
14.
0.882
53000.0
0.575
10.5
.1
,7
12.06,
55'
5.26
1.59,
4.07
0.0
0.30
8.97J
93.37;
14.59*
-------
Table 12 (Continued). CORN FORAGE YIELD, UPTAKE BY CORN
OF INDICATED ELEMENTS, CORN PLANT POPULATION, NITRATE -N CONTENT OF CORN FORAGE,
AND ELECTRICAL CONDUCTIVITY OF SURFACE SOIL SATURATION EXTRACTS AS AFFECTED BY ACCUMULATIVE
YEARLY APPLICATIONS OF BEEF FEEDLOT MANURE (DRY MT/ha.) THAT BEGAN IN THE FALL OF 1969
Measurement
Yield (MT/ha.)
N uptake (kg/ha.)
P uptake (kg/ha.)
K uptake (kg /ha.)
Ca uptake (kg/ha.)
Mg uptake (kg/ha.)
Na uptake (kg/ha.)
Population (No. /ha.)
Spring Soil EC (mmho/cm)
Fall Soil EC (mmho/cm)
Forage Nitrate-N (ppm)
Yield (MT/ha.)
Population (No. /ha.)
Spring Soil EC (mmho/cm)
Forage Nitrate-N (ppm)
a
Data are expressed as
** r« J .1 .C J _ __ j_ „ *. ^t. A rt T
R2
0.480
0.108
0.084
0.024
0.156
0.165
0.088
0.355
0.840
0.804
0.178
0.512
0.308
0.882
0.142
factors of a
1C 1 „.,„-!
a
a
1972
**— —
-0.0000278
-0.00000739
-0.0000176
0.000000408
b
-0.000562°
1973
-0. 000009 30b
-•• ~~™"
regression equation
ba
-0.0153b
0.0304
0.00971
0.0170
-0.00678?
-0.00313
-0.000549
-2.80b
0.00785?
0.00362
1.10
0.0139
-*•" b
0.00390°
r
0.128b
2
y = ax
a
c
60.2
183.0
37.1
251.0
29.7
18.9
0.921
57400.0
0.580
0.554
518.0
42.4
45900.0
0.195
376.0
+ bx + c
F
24.03b
1.52
1.14
0.31
4.81b
5.14°
1.20
14.28b
136. OIT
106. 44D
2.71
13.10b
11.59J
194.71
4.30°
-------
SPRING 1972
CONTROL
90 MT/Hfl.
175
400
573
985
1878
300
60 120 180
NlTRflTE-N. PPM
FflLL 1972
240
300
90 MT/HR.
175
MOO
573
985
1878
300
40'60'80
NnRRTE-NITROGEN. PPM
100
Figure 14. Nitrate-N content of soil cores as affected by depth and
average accumulative applications of beef feedlot manure
(dry weights) that began in 1969.
54
-------
SPRING 1970
t—
0.
CONTROL
58 MT/HR.
85
202
372
595
1043
60
100-
mo 210
flMMONIUM-N. PPM
SPRING 1971
280
350
ino
0
Figure 15. Ammonium-N content of soil cores as affected by depth and
average accumulative applications of beef feedlot manure
(dry weights) that began in 1969.
.55
-------
FFILL 1972
20
40-
60-
60
100
o
20-
40-
60-
80
100
X X
CONTROL
90 MT/Hfl.
175
400
573
985
1878
350 700
EXTRfiCTflBLE
1050 1400
POTRSSIUM. PPM
1750
FflLL 1972
liO ' 120 ' 180
EXTRnCTRRLE SOD1UH. PPM
240
300
Figure 16.
Extractable Na and K of soil cores as affected by depth
and average accumulative applications of beef feedlot
manure (dry weights) that began in 1969.
56
-------
FRLL 1972
o
Q—£3 CONTROL
e—e> 90 MT/Hfl.
175
400
573
985
1878
100
9*0 180 270 360
EXTRfiCTRBLE PHOSPHORUS. PPM
450
Figure 17. ExtractabJe P of soil cores a» affected by depth and aver-
age accumulative applications of beef feed.Lot manure (dry
weights) that began in 1969.
57
-------
treatment was supplying N in excess of what could be removed by the corn
forage. This excess N was nitrified into NO^-N and became subject to
leaching. The concentrations of NO~-N in the surface 30 cm of the
spring 1972 cores show that large amounts of this anion had come into
the soil solution. Leaching by irrigation water and plant uptake had
lowered the surface 30-cm concentrations by the fall of 1972. Relative
to that found under the control plots, all treatments except the lowest
one showed evidence of having caused NO^-N movement to 160 cm in the
fall 1972 cores. Less well defined peaks are found at the 200-cm depth
of the spring and fall 1972 cores taken from plots receiving the heav-
iest treatment. NOg-N analysis of cores taken in 1970 and 1971 show
accumulations and sequential movement (to 160 cm) that were both gen-
erally greater under plots receiving the two heavier treatments.
Ammonium -N concentrations were found to be high in the surface 30 cm of
cores taken in the spring (Figure 15). Ammonium toxicity could have
been a contributing factor in lowered plant populations in some years
(Figure 18). Extractable K content of soil cores was not affected by
the lowest treatment at any date. All higher treatments caused accumu-
lations of K in the surface 30 cm, the magnitudes being greater under
the higher treatments. K increased at the 50-cm depth under plots
receiving the heaviest treatment at the fall 1971 and 1972 (Figure 16)
samplings. Movement of K was probably restricted by cation-exchange
reactions. Na is less competitive for cation exchange sites and was
leached to lower depths. Analysis of the fall 1972 cores shows that all
treatments had increased Na throughout the top meter relative to the
control (Figure 16). No trend due to treatment could be found in the
analysis of soil cores for extractable Ca or Mg.
Extractable P was found to have accumulated in the fall 1972 cores at
the 10-cm depth at all treatment rates, and at the 30-cm depth in plots
receiving the highest treatment (Figure 17). The lack of P movement
below 30 cm indicates that the capacity of the soil to immobilize the
added P had not yet been exceeded.
Effects of Yearly Treatments on Corn
Corn forage yield was enhanced by the lower and intermediate treatments
and depressed by the higher treatments all four years (Figure 19). This
quadratic effect was least apparent in the 1972 yields. The positive
effect on yield can be explained by improved soil fertility since no
nutrients were added to control plots. The negative effect was probably
due to the salt buildup in the soils receiving the heavier treatments.
The depression of yield by the higher rates in 1970, 1972, and 1973
could partially be explained by lowered germination and/or seedling
growth because corn plant populations were decreased in those years
(Figure 18). Maximum yields, predicted from yield equations given in
Table 12, occurred at accumulative application rates of 230, 300, and
747 MT/ha. in 1970, 1971, and 1973, respectively. These application
rates are equivalent to applications of 230, 150, and 187 metric tons
58
-------
FRLL 1970
600
o
x
.«8C
Sna
cc
cr
-360-
240-
£C
O
U
120
"i^&o o •
a B
D a
125'250'iTi'560
MRNURE flPPLICflTION. MT/Hfl-
FflLL 1972
625
-350-
z
tz
c:
o
o
120
500 1000 1500 2000 25'OU
BCCUKULtUIVE MflNURE flPPLICflTION. MT/Hfl.
FflLL 1971
600-1
120
0 "2?0'5^0'7?01000 ' 1250
RCCUMULflTIVE MRNURE flPPLlCRTION. MT/Hfl.
FflLL 1973
600
1200
1800 2400 3000
flCCUMULflTIVE MflNURE BPPLJCBTION, MT/HA,
Figure 18. Corn plant populations as affected by accumulative applications of beef feedlot manure
(dry weights) that began in 1969.
-------
FflLL 1970
FflLL 1971
80-
d
*60-
UJ
u
-------
per hectare per year (MT/ha./yr) in 1970, 1971, and 1973, respectively.
Maximum yields cannot be expected to continue at these rates, however,
because saline soil conditions would eventually be created. By
inspection of Figures 13 and 19, it can be seen that near maximum yields
were recorded from the eight plots receiving the lowest treatments and
that significant salt buildup had not occurred at these rates (29 - 68
MT/ha./yr after 4 years) by the spring of 1973. Continued study will be
needed to determine if these rates can be maintained without deleterious
effects on forage yields.
Uptake of N, P, K, and Ca in 1970 and N and P in 1971 was quadratically
related to accumulative treatment as was yield in those years (Figure 20
and Table 12). Mg uptake in 1970 and Ca and Mg uptake in 1972 were
linearly depressed by manure treatments. These data show that removal
of these elements from the soil can be reduced by heavy applications of
manure that reduce corn forage production. Na uptake was not found to
be affected by manure treatment.
NO~-N content of corn forage was a quadratic function of treatment in
1971 and 1972 and a linear function in 1973 (Figure 21). In 1972,
forage NO^-N concentrations from plots receiving accumulative manure
applications of from 124 MT/ha. (41 MT/ha./yr) to 631 MT/ha. (210
MT/ha./yr) generally exceeded 700 ppm NO~-N, a known level at which
animal toxicity can occur if ingested (Gardner68).
Effects of Residual Treatments on Soil Chemical Properties
EC analysis of surface soil samples taken in the fall of 1972, three
years after the manure was applied, showed residual accumulations of
soluble salts (Figure 22). The EC values were lower than those measured
in 1970 (Figure 13) indicating that leaching and plant uptake had re-
moved much of the salts out of the surface 15 cm. By the spring of 1973
there was little relationship between surface EC and treatment (Table
13).
In the two replications where soil cores were taken, the four plots that
were intended to receive the two lower residual treatments received
actual tonnages that were so close together that, for practical compara-
tive purposes, they could not be separated. The data presented in
Figures 23 and 24 are based on a control and two residual treatments:
control, an average of data from two plots; 230 MT/ha., an average from
four plots; and 481 MT/ha., an average from two plots. Data from ad-
jacent depth increments were combined in the same manner described for
the yearly treatments.
In the fall 1972 cores, no differences between the two residual treat-
ments and the control were found in the extractable Na content at the
10-cm depth (Figure 23). Higher concentrations of Na were found at
depths below 10 cm under plots receiving residual manure treatments than
under control plots. This indicates that in three years most of the
61
-------
320
cr
x
V.
oc
H- •
a.
^>
UJ
o
cc
80: :x
0
FflLL 1971
x x
0 250 500 750 1000 1250
flCCUMULflTIVE MflNURE flPPLICflTIGN, MT/Hfl.
FflLL 1971
0 250 500 750 1000 1250
flCCUMULflTIVE MflNURE RPPLICflTION. MT/Hft.
Figure 20. Uptake of N and P by corn forage as affected by accumula-
tive applications of beef feedlot manure (dry weights)
that began in 1969.
62
-------
ecoo
,1500-
^1000-
5CO-
FflLL 1972
"0 450 900 1350 18'00 2250
fiCCUrtULRTIVE MflNURE flPPlICRTIQN. MT/Hfl.
FflLL 1971
.300-
CL.
Q.
,200-
cr
cc
:IOQ-
"0 250 500 750 1000 1250
RCCUHULRTIVE HfiNURE RPPL1CRTICN. HT/HR.
FflLL 1973
1600-
.1200-
o.
o_
J, 800^
X I
"0 550 1100 1550 2200 2750
RCCUMULRTIVE MfiNURE RPPLICftTlON. MT/HR.
P'igure 21. Nitrate-N content of corn forage (dry weight basis) as affected by accumulative appli-
cations of beef feedlot manure (dry weights) that began in 1969.
-------
UJ
0
FRLL 1972
375 500
HRNURE RPPLICRTIQN. MT/Hfl.
625
Figure 22. Electrical, conductivity of water Mat urn Lett pasti- ojctrv*rts
from surface (0 to 15 cm) soli sampJes as affected by n
single application of beef feediot manure: (dry weights) in
1969.
-------
Table 13. CORN FORAGE YIELD, UPTAKE OF INDICATED
ELEMENTS, CORN PLANT POPULATION, NITRATE-N CONTENT OF CORN
FORAGE, AND ELECTRICAL CONDUCTIVITY OF SURFACE SOIL SATURATION EXTRACTS
AS AFFECTED BY A SINGLE APPLICATION OF BEEF FEEDLOT MANURE (DRY MT/ha.) IN THE FALL OF 1969
Measurement
Yield (MT/ha.)
N uptake (kg/ha.)
P uptake (kg/ha.)
K uptake (kg/ha.)
Ca uptake (kg/ha.)
Mg uptake (kg/ha.)
Na uptake (kg/ha.)
Population (No. /ha.)
Fall Soil EC (mmho/cm)
Forage Nitrate-N (ppm)
Yield (MT/ha.)
N uptake (kg/ha.)
P uptake (kg/ha.)
K uptake (kg/ha.)
Ca uptake (kg/ha.)
Mg uptake (kg/ha. )
Na uptake (kg/ha. )
Population (No. /ha.)
Spring Soil EC (mmho/cm)
Fall Soil EC (mmho/cm)
Forage Nitrate-N (ppm)
R2
0.211
0.268
0.230
0.013
0.109
0.239
0.159
0.381
0.365
0.626
0.163
0.529
0.543
0.314
0.039
0.014
0.008
0.041
0.651
0.422
0.231
a
a
1971
-0.0000991
-0.000444
-0.0000534
-0.000427
-0.0000703
-0.0000555
-0.00000789
1972
-0.0000561
-0.000675b
-0.000135b
0.0000424
___
—
-0.00393
ba
0.0638
0.350
0.0552
0.216
0.0458
0.0343
0.00380
-6.36b
0.00144°
0.746°
0.0364
0.475b
0.0970
0.171°
-0.0181
0.00319
-0.000117
2.26
0.00169°
0.000825
3.61
a
c
34.1
117.0
23.5
253.0
0.109
13.8
0.814
0.381
0.819
-7.34
54.8
136.0
28.3
195.0
27.3
18.4
0.670
56300.0
0.797
0.825
118.0
F
1.74
2.42
1.97
0.09
0.83
2.14
1.24
8.62°
. n
8.04J
23.44
1.27
7.30b
7.73b
6.41
0.26
0.20
0.12
0.60
26.17b
10.20
1.95
-------
Table 13 (Continued). CORN FORAGE YIELD, UPTAKE OF
INDICATED ELEMENTS, CORN PLANT POPULATION, NITRATE-N CONTENT OF CORN
FORAGE, AND ELECTRICAL CONDUCTIVITY OF SURFACE SOIL SATURATION EXTRACTS
AS AFFECTED BY A SINGLE APPLICATION OF BEEF FEEDLOT MANURE (DRY MT/ha.) IN THE FALL OF 1969
Measurement
Yield (MT/ha.)
Population (No. /ha.)
Spring Soil EC (mmho/cm)
Forage Nitrate-N (ppm)
a Data are expressed as
R2
0.686
0.011
0.121
0.147
factors of a
\ C 1 1
aa
1973
-0.000106b
18.9
regression equation:
ba ca F
0.0947b 32.0 14.19b
-2.08 44600.0 0.15
0.000807 1.04 1.92
-0.871 284.0 1.12
2
y = ax + bx + c.
-------
FflLL 1972
20-
z:
i-
o.
60-
80
19—D CONTROL
x—X 230 MT/Hfl-
»—* 1181 MT/Hfl.
>00 300 400 500 600
EXTRflCTRBLE POTRSSIUM, PPM
FflLL 1972
700
20-
5
60
80
100
o—E CONTROL
x—x 230 MT/Hfi-
U81 MT/Hfl.
0 60 120 180 2'10
EXTRflCTRRLE SODIUM. PPM
300
Figure 23. Extrar.tablu Na and K <:ontc-nt of soil cori^s ;is nl f ccl cil by
depth and a single app 1 ir;it_ Ion of" bccT I'ft-dloL manure (dry
weights) in 1969.
67
-------
FflLL 1972
20-
o
•
3:
i—
Q_
60-
80
100
;i20
11 BO
240
300
CONTROL
x—x 230 M7/HR-
•»—» U81 MT/Hfl.
0 "" 50 ' 100 ' 150 ' 200 ' 250
EXTRflCTRBLE PHOSPHORUS. PPM
FflLL 1972
0—B CONTROL
x—x 230 MT/Hfl-
481 MT/Hfl.
"i ' To 20
NITRflTE-NITRnGEN. PPM
Figure 24. Nitrate-N and extractable P content of soil cores as
affected by a single application of beef feedlot manure
(dry weights) in 1969.
68
-------
applied Na had been leached from the surface 20 cm and transported to
lower depths with maximum movement of at least one meter. By the fall
of 1972, K had showed no movement below the 50-cm depth (Figure 23) and
P had no movement below the 30-cm depth (Figure 24). The fall 1972
cores showed increases of NO^-N at the 160-cm depth under plots that had
received 230 MT/ha. and at the 200-cm depth under plots that had re-
ceived 481 MT/ha. (Figure 24). No trend due to treatment could be found
in the analysis of soil cores for extractable Ca or Mg.
Effects of Residual Treatments on Corn
Residual positive effects on soil fertility were expressed as increased
corn forage yield in 1973, four years after the application of manure
(Figure 25). Less consistent quadratic trends were found in the 1971
and 1972 yields (Table 13). A negative effect on corn plant population
was still evident in 1971, two years after manure applications, but an
effect was not found in 1972 or 1973 indicating that leaching of salts
from the surface soil or lowered ammonification had been sufficient by
1972 to prevent germination damage.
The NO^-N concentrations of the 1971 corn forage were increased linearly
by residual treatment but were not raised to toxic levels. Increases in
NO~-N concentrations in the 1972 and 1973 forage were not consistent
with treatment, but potentially toxic levels (747 to 1160 ppm) were
found in the 1972 forage from five plots receiving residual treatments.
69
-------
FflLL 1973
60
250 375 500 625
MRNURE flPPLICflTlON, MT/HR.
Figure 25. Corn forage yield (corrected to 30% dry matter) four years
after a single application of beef feedlot manure (dry
weights) in 1969.
70
-------
SECTION X
MICRONUTRIENT RELATIONSHIPS TO LAND DISPOSAL OF FEEDLOT WASTES
GENERAL
Efficient utilization of plant nutrients contained in animal manures
should be an important consideration when disposing of these wastes onto
soil. The effects of beef feedlot manure and lagoon water on concentra-
tions of Fe, Zn, Mn, and Cu in corn forage, and on levels of Diethylene
Triamine Penta Acetic Acid (DTPA) extractable Fe, Zn, Mn, and Cu in the
soil were investigated.
METHODS AND PROCEDURES
The micronutrient study was conducted on selected plots in the waste
disposal study area described in Sections VIII and IX of this report.
Applied wastes were analyzed for Fe, Zn, Mn, and Cu by atomic absorption
techniques after a nitric-perchloric acid digestion.
In the fall of 1971, soil cores were taken by stainless-steel tubing to
one meter from three control plots (no waste or chemical fertilizer), 12
plots (representing six treatments) that had received yearly manure
applications for two years, six plots (representing two treatments) that
received manure application two years previously, and eight plots (re-
presenting four treatments) that received two years of lagoon water
treatments. These cores were divided into 10-cm increments and analyzed
for DTPA-extractable Fe, Zn, Mn, and Cu using the procedure outlined by
Lindsay and Norvell69 Atomic absorption techniques were used for the
extract analysis. The pH of selected soil cores that had received
yearly manure applications was measured using a 1:1 soil water ratio.
Corn forage yield measurements (corrected to 30% dry matter) and corn
forage samples were taken in the summers of 1970, 1971, and 1972. Corn
leaf samples (June 15 to July 15) were taken in 1970, 1971, and 1972
from plots receiving manure. The plant samples were analyzed by atomic
absorption for Fe, Zn, Mn, and Cu after a nitric-perchloric acid di-
gestion.
71
-------
RESULTS AND DISCUSSION
Waste Analysis and Soil pH
Table 14 gives the average analysis of the manure and lagoon water
applied to the disposal plots for total Fe, Zn, Mn, and Cu. Measure-
ments of pH of selected soil cores taken from plots before and after
they had received two years of manure applications are given in Table
15. Only very small increases or no change in pH were found, indicating
that effects of manure on plant-nutrient availability probably would
not be related to alterations of soil pH.
Table 14. AVERAGE ANALYSIS OF BEEF FEEDLOT MANURE AND
LAGOON WATER APPLIED TO DISPOSAL PLOTS
Iron
ppm
Zinc
ppm
Manganese
ppm
Copper
ppm
1969 Average
1971 Average
1972 Average
Sample High
Sample Low
3-Year Average
Manure (dry weight basis)
8820
4810
5810
10300
3000
6480
66.0
55.6
46.6
120.0
35.7
56.1
106
192
234
43
149
Lagoon water (wet weight basis)
12.
20.
29.
10.
16.
1972 Average
Sample High
Sample Low
1.8
2.2
1.3
0.14
0.19
0.05
0.29
0.34
0.25
0.51
0.55
0.40
Table 15. THE pH (1:1 SOIL TO WATER RATIO) OF SELECTED SOIL CORES
Depth
cm
Date:
0-10
10-20
20-30
30-40
40-50
Average accumulative manure treatment
0
1969
7.1
7.0
7.1
7.1
7.6
1971
7.2
7.0
7.0
7.1
7.4
85
1969
7.0
6.4
7.0
7.2
7.3
1971
7.2
7.1
7.2
7.2
7.4
372
1969
7.2
7.0
7.3
7.5
7.9
(MT/ha. )
1040
1971
7.3
7.3
7.4
7.5
7.6
1969
7.0
7.1
6.9
6.8
7.0
1971
7.2
7.2
6.9
7.0
7.4
72
-------
Iron
Increased DTPA-extractable Fe was found as deep as 15 and 25 cm in soil
cores taken from plots that had received accumulative yearly manure
applications of 595 and 1043 dry MT/ha., respectively, relative to cores
from control plots. Lower yearly treatments had little effect on DTPA
Fe. The 481 MT/ha. residual manure treatment increased Fe to 15 cm,
while the three highest lagoon water treatments increased Fe at the 5-cm
depth with erratic response below 15 cm (Figure 26). Based on these
data, high rates of manure and, to a lesser extent, lagoon water will
increase the availability of Fe as measured by the DTPA extraction. The
much lower amounts of total Fe being added through the lagoon water
(Table 14) explains the lesser response of lagoon water on DTPA Fe.
Results of regression analyses on Fe uptake and corn leaf and forage
content of Fe are given in Tables 16-18. Fe uptake was not affected by
either yearly or residual manure treatments, but was increased by lagoon
water linearly in 1970 and quadratically (increased uptake at the inter-
mediate rates and relative decline at the higher rates) in 1971 as was
forage yield in those years (Table 18). Forage or leaf Fe content was
not consistently related to any type of waste treatment.
The levels of DTPA-extractable Fe measured on all plots, including
controls, were higher than 0.25 ppm which is considered to be a critical
level below which Fe deficiencies might occur (Whitney et al.70). Even
though the three types of waste treatments did increase available Fe
concentrations in the soil, there was evidently so much Fe originally
present that corn Fe content and uptake were not affected.
Zinc
All yearly manure treatments increased DTPA Zn at the 5-cm depth and the
four highest yearly treatments increased Zn at the 15-cm depth relative
to control plots. The residual manure and lagoon water treatments
increased DTPA Zn at the 5-cm and 15-cm depths (Figure 27). These data
show that the availability of Zn as measured by the DTPA extraction was
increased by all waste treatments.
The levels of Zn measured in soils of the control plots were close to
0.5 ppm which is considered to be the critical Zn level below which Zn
deficiencies are likely to occur (Whitney et al.70). Increased avail-
ability in the soil was reflected in some years by higher Zn concen-
trations in corn leaf and forage that had received yearly manure applica-
tions (Table 16 and Figure 28). Residual manure or lagoon water had no
consistent effect on Zn content of corn leaf or forage (Tables 17 and
18), and Zn uptake was not affected by any type of waste treatment
(Tables 16-18).
73
-------
«>
eo
100
100
£; to
BO
ri—fi CONTI10I
o—6 LH HI /HO.
x—K ?6?
•—» 372
«— K S'JS
«—« 10'13
24 36
FE. PPH
RESIOUF)L MRNURt:
12 18 24
FE. PPM
LRGOON HflTF.R .
r» P) COHllim.
• • M CM/TLflH
« - » 1 b
43
12 18
FE. PPH
24
30
Figure 26. DTPA extractable Fe as affected by depth and applications
of beef feedlot wastes.
74
-------
Table 16. CORN FORAGE YIELD, COMPOSITION AND UPTAKE OF INDICATED
ELEMENTS AND CORN LEAF TISSUE COMPOSITION AS AFFECTED BY ACCUMULATIVE YEARLY
APPLICATIONS OF BEEF FEEDLOT MANURE (DRY MT/ha.) THAT BEGAN IN THE FALL OF 1969
Forage yield (MT/ha.)
Forage composition
Fe (ppm)
Zn (ppm)
Mn (ppm)
Cu (ppm)
Forage uptake
Fe (kg/ha.)
Zn (kg/ha.)
Mn (kg /ha.)
Cu (kg/ha.)
Tissue composition
Fe (ppm)
Zn (ppm)
Mn (ppm)
Cu (ppm)
Forage yield (MT/ha.)
Forage composition
Fe (ppm)
Zn (ppm)
Mn (ppm)
Cu (ppm)
R2
0.248
0.027
0.011
0.524
0.020
0.102
0.017
0.496
0.062
0.260
0.216
0.732
0.018
0.491
0.065
0.497
0.551
a
a
1970
-0.000 12 7b
-0.000121
0.0000229
v^
-0.00000564
-O.OOOOOQ597
-0.000000274
-0.0000060
1971
-0.0000446b
b
0.0000158
faa
0.0583b
0.0831
-0.0108,
0.0967
0.00164
0.00287
0.000307
0.00103b
0.000145
u
0.0939°
0.0180
0.152b
0.00369
0.0268
0.0175
-0.00854
0.0289b
a
c
45.4
113.0
20.3
27.5
6.75
1.57
0.266
0.448
0.0922
119.0
22.8
43.9
8.76
37.5
95.7
17.5
33.5
F
6.10b
0.51
0.20
41.90
0.41
2.53
0.32
37.42b
1.22
V,
13.35b
10.44:
103.67°
0.33
12.06b
0.87
12. 36*
31.93
-------
Table 16 (Continued). CORN FORAGE YIELD, COMPOSITION AND UPTAKE
OF INDICATED ELEMENTS AND CORN LEAF TISSUE COMPOSITION AS AFFECTED BY ACCUMULATIVE
YEARLY APPLICATIONS OF BEEF FEEDLOT MANURE (DRY MT/ha.) THAT BEGAN IN THE FALL OF 1969
Forage uptake
Fe (kg/ha. )
Zn (kg/ha.)
Mn (kg/ha.)
Cu (kg/ha.)
Tissue composition
Fe (ppn)
Zn (ppm)
Mn (ppm)
Cu (ppm)
Forage yield (CT/ha.)
Forage cocpositicn
Fe (ppm)
Zn (ppn)
Mn (ppn)
Cu (ppm)
Forage uptake
Fe (kg/ha. )
Zn (kg/ha. )
Mn (kg/ha. )
Cu (kg/ha.)
Tissue composition
Fe (ppm)
Zn (ppm)
Mu (ppm)
Cu (ppm)
R2
0.243
0.175
0.396
—
0.003
0.084
0.621
0.239
0.480
0.195
0.207
0.472
0.097
0.056
0.010
0.040
0.005
0.047
0.566
0.608
0.139
a*
-0.00000154
-0.00000014
-0.00000100
—
-0. 0000589b
—
1972
___
0.0000400
- —
—
-0.0000000686
0.00000152
b*
0.00112
0.0000900
0. 00099 3b
— —
-0.00566
0.00433
0.0875b.
-0.00305"
-0.0153b
-0.0481
0.00885
0.01580
0.00217
-0.000335
-0.0000324
0.000165
-0.00000741
0.00969.
0.00729
0.0163b
-0.00312
a
1.09
0.192
0.349
«_
111.0
20.6
34.6
8.24
60.2
125.0
21.4
20.0
4.45
2.07
0.411
0.367
0.0820
108.0
29.3
36.0
9.02
F
b
4.00
2.64.
8.24b
«w
0.07
2.39.
20.45b
n
8.18
24.03b
3.03
6.79°
23.306
2.80
1.55
0.26
0.53
0.13
1.29
33.85J
40. 30
2.01
Data are expressed in the form of a regression equation: y » ax •+• bx + c
Significant at the 0.05 level.
-------
Table 17. CORN FORAGE YIELD, COMPOSITION AND UPTAKE OF INDICATED
ELEMENTS AND CORN LEAF TISSUE COMPOSITION AS AFFECTED BY A SINGLE
APPLICATION OF BEEF FEEDLOT MANURE (DRY MT/ha.) IN THE FALL OF 1969
Forage yield (MT/ha.)
Forage composition
Fe (ppm)
Zn (ppm)
Mn (ppm)
Cu (ppm)
Forage uptake
Fe (kg/ha.)
Zn (kg/ha.)
Mn (kg/ha.)
Cu (kg/ha.)
Tissue composition
Fe (ppm)
Zn (ppm)
Mn (ppm)
Cu (ppm)
Forage yield (MT/ha. )
Forage composition
Fe (ppm)
Zn (ppm)
Mn (ppm)
Cu (ppm)
R2
0.211
0.010
0.393
0.306
0.132
0.090
0.224
0.041
0.341
0.485
0.394
0.163
0.325
0.039
0.065
0.083
a
a
1971
-0.0000991
-0.0000364
___
-0.00000347
-0.00000038
-0.00000084
~~~™ h
0.000125
~™~ h
-0.0000271
1972
-0.0000561
0.0004163
0.0000334
-0.0000244
b3
0.0638
0.0243 ,
-0.00823
-0.0163b
0.00226
0.000163
0.000755
0.0168
-0.0575
0.0253a
0.0186a
0.0364
-0.250a
-0.0145
0.00775
0.0128
a
c
34.1
94.4
18.5
31.8
0.965
0.195
0.332
95.4
23.0
33.2
5.85
54.8
130.0
19.2
19.0
5.28
F
1.74
0.07
9.07a
6.16a
1.02
0.63
1.92
0.60
3.37
13'20b
4.23b
1.27
3.12
0.26
0.98
0.59
-------
00
Table 17 (Continued). CORN FORAGE YIELD, COMPOSITION AND UPTAKE
OF INDICATED ELEMENTS AND CORN LEAF TISSUE COMPOSITION AS AFFECTED
BY A SINGLE APPLICATION OF BEEF FEEDLOT MANURE (DRY MT/ha.) IN THE FALL OF 1969
Forage uptake
Fe (kg /ha.)
Zn (kg/ha.)
Mn (kg/ha.)
Cu (kg/ha.)
Tissue composition
Fe (ppm)
Zn
Mn,
Cu
(ppm)
(ppm)
(ppm)
R2
0.147
0.019
0.058
0.122
0,267
0.334
0.039
0.443
a
a
1972 (Continued)
0.00000572
-0.000000550
-0.000139
0.0000491
-0.0000176
0.0000181
ba
-0.00338
0.0000987
0.000158
0.000303
0.108
-0.0347
0.00854
-0.0157b
c
2.19
0.310
0.330
0.0855
92.4
31.8
35.3
10.1
F
1.12
0.27
0.87
0.90
2.37
3.27
0.26.
5.16b
2
Data are expressed in the form of a. regression equation: y - ax + bx + c
Significant at the 0.05 level.
-------
Table 18. CORN FORAGE YIELD, COMPOSITION AND UPTAKE OF
INDICATED ELEMENTS AS AFFECTED BY ACCUMULATIVE YEARLY APPLICATIONS
OF BEEF FEEDLOT LAGOON WATER (cm) THAT BEGAN IN THE SUMMER OF 1970
R
1970
VO
Forage yield (MT/ha.) 0.316
Forage composition
Fe (ppm) 0.019
Zn (ppm) 0.095
Mn (ppm) 0.003
Cu (ppm) 0.092
Forage uptake
Fe (kg/ha.) 0.283
Zn (kg/ha.) 0.080
Mn (kg/ha.) 0.060
Cu (kg/ha.) 0.453
Forage yield (MT/ha.) 0.372
Forage composition
Fe (ppm) 0.365
Zn (ppm) 0.10 7
Mn (ppm) 0.444
Cu (ppm) 0.528
Forage uptake
Fe (kg/ha.) 0.453
Zn (kg/ha.) 0.116
Mn (kg/ha.) 0.218
Cu (kg/ha.) 0.425
-0.0367
-0.000581
1971
-0.004lOb
-0.00634
0.000521
-0.000487
-0.000178b
-0.0000130
-0.0000109b
0.498"
-0.314
1.22
-0.0381
-0.0195
0.0161b
0.0228
0.00339
0.000949
0.425
0.993b
-0.0372
0.171b
0.0791
0.0219b
0.00145
0.00205^
0.00141b
41.5
141.0
22.8
33.1
4.52
1.70
0.282
0.432
0.0561
8.30U
0.35
0.06
1.81
7.11b
1.15,
K
14.89
36.3
5.04C
69.8
16.7
33.2
3.61
0.759
0.184
0.426
0.0424
4.88U
1.02,
K
14.36^
9.50b
9.95b
1.75,
7.14b
8.54b
-------
00
o
Table 18 (Continued). CORN FORAGE YIELD, COMPOSITION AND
UPTAKE OF INDICATED ELEMENTS AS AFFECTED BY ACCUMULATIVE YEARLY
APPLICATIONS OF BEEF FEEDLOT LAGOON WATER (cm) THAT BEGAN IN THE SUMMER OF 1970
Forage yield (Ml/ha.)
R2
0.269
a
1972
-0.00322b
ba
0.426b
Forage composition
Fe
Zn
Mn
Cu
(ppm)
(ppm)
(ppm)
(ppm)
0.015
0.176
0.489
0.223
-0.000448
0.112
-0.0256
0.123b
0.0667
a
c
49.2
157.0
19.0
28.3
3.96
Forage uptake
Fe
Zn
Mn
Cu
(kg/ha.)
(kg/ha. )
(kg/ha. )
(kg/ha.)
0.156
0.162
0.486
0.305
-0.000164
-0.0000153
-0.0000389
-0.0000121
0.0237
0.00163
0.00 713:'
0.00171
2.27
0.285
0.399
0.0600
F
3.13
0.28
3.84
17.22°
2.44
1.60
1.64,
8.04b
_ n
3.73
Data are expressed in the form of a regression equation: y - ax + bx + c
Significant at the 0.05 level.
-------
MflNUnE
B-e CONlttOL
o—o 58 Ml/llfl.
•—» B'j
x—K 202
«—> 372
x —K S95
»—« 10'13
3
ZN. PI'n
C.O
60
BO
0—0 CONTROL
230 M7/HH.
481
lOgl
0.1 0.8 1.2 1.6
ZN. PPM
2.0
LRGOON HRTER
B—o CONTHOL
«—» 8 CM/Ttnn
i—x 15
x—K 23
• —« 43
0.3
r
-------
00
t\>
1970 TISSUE
125
250 375 ' 500 ' 65
RPPLlCflTlON.
1971 FGRRGE
2SC SCO 750 1000 1250
, MT/H3.
56
197? TISSUE .
US'
a.
Q-,i
32-
x x
50C 1000 15CO 2000 25CO
E MRNl'RE RPPLlCflTlC^. MT/Hfi.
1972 FORRGE ,_
"0 560 1000 1500 2000 2500
RCCimULRtlVE MflNURE RPPLICflTICN. MT/Kfl.
Figure 28. Zinc concentrations in corn leaf tissue and corn forage as affected by accumulative
yearly applications of beef feedlot manure (dry weights) that began in 1969.
-------
Manganese
DTPA-extractable Mn was found to be at high concentrations at depths of
from 15 to 50 cm under plots receiving the highest yearly manure treat-
ment but this trend was not present in plots receiving the second high-
est yearly manure treatment (Figure 29). Increased DTPA Mn was found,
relative to control plots, at the 15-and 25-cm depths in cores taken
from plots receiving all yearly manure treatments except the lowest and
the second highest. Residual manure treatments had little effect on
DTPA Mn, while all lagoon-water treatments increased Mn at the 5-cm
depth (Figure 29). These data show that applications of beef f eedlot
wastes can increase DTPA-extractable Mn in soil.
Manganese content in corn was more correlated to waste treatment than
any of the four elements measured. Forage and leaf content of Mn was
increased at all sampling dates by the yearly manure treatments (Figure
30 and Table 16). Residual manure treatments caused inconsistent re-
sponse in corn Mn content: 1971 forage Mn content was linearly depressed
by treatment while 1971 leaf content was linearly increased (Table 17).
Lagoon-water treatments linearly increased Mn in the 1971 and 1972 corn
forage (Figure 31 and Table 18). Increased forage Mn content masked
relative yield depression by the higher yearly manure treatments in 1970
and by the higher lagoon-water treatments in 1971, which resulted in
linear Mn uptake response in these years when the yield response was
quadratic. Mn uptake did, however, have similar quadratic responses as
those of yield in 1971 from plots receiving yearly manure and in 1972
from plots receiving lagoon water (Figures 32 and 33 and Tables 16 and
18).
The DTPA Mn data and, to a greater extent, the plant Mn data show that
manure and lagoon water increased the availability of Mn in the soil.
In other work (Hensler et _al• ,**6'**7 Atkinson _et al.,48 Page5**), Mn
became less available when manure was applied; the lowered availability
was attributed to a liming effect of the manure which raised soil pH and
lowered the solubility of Mn compounds. Inorganic Mn equilibria has
been reviewed by Lindsay.29 Since the soil in this study was neutral to
basic before manure applications and pH was not appreciably raised by
the manure, a factor other than pH must have influenced Mn availability.
This factor could have been the creation of reducing conditions in the
soil during and after irrigations when waterlogged soil conditions along
with organic matter decomposition would lower the oxygen supply and EC.
Meek et al.71 found increased Mn and Fe in soil solutions when an or-
ganic^matter-amended calcareous soil was flooded. Soils conditions
similar to those measured by Meek e^ al.71 would probably have been
created in this study by feedlot waste applications and irrigations with
the resultant increase of the reduced Mn+2 form in solution.
83
-------
Eh—n CON I HOI
8 CM/TtHH
1—« 15
23
12 2'l 36 K8 CO
10O
Figure 29. DTPA extractable Mn as affected by depth and applications
of beef feedlot wastes.
84
-------
1970 TISSUE
200
150-
100-
2
I
50*.
x
x
100-
eo-
1971 TISSUE
Q-
Q_
0 125 250 375 500 625
RCCUKULRTIVE MRNURE RPPUCRT I ON. MT/Hfi.
1972 TISSUE
0 250 500 750 1000 1250
RCCUMULRTIVE MflNURE RPPLICRTION. MT/HR.
100-
1971 FCRRG
a.
Q_
SCO 1000 1500 2000 2500
RCCUMULRTIVE KflNURE fiPPLICRTION. MT/HR. RCCUMULRTIVE MflNURE RPPLICRTION. MT/HR.
Figure 30. Manganese concentrations in corn leaf tissue and corn forage as affected by accumulative
yearly applications of beef feedlot manure (dry weights) that began in 1969.
-------
1971 FORRGE
"0 22' 4U ' 66 88 liO
RCCUMULflTIVE LflGOON WflTER RPPLICRTION. Ch
1972 FGRRGE
"0 30 60 90 120 150
flCCUMULRTIVE LRGOGN WflTER RPPLICRTIQN, CM
Figure 31. Manganese concentrations in corn forage as affected by
accumulative yearly applications of beef feedlot lagoon
water that began in 1970.
-------
1970 YIELD
80-
1971 YIELD
"0 125 250 375 SCO 625
RCCUMJLflTIVE MRNURE RPPLICRTION, MT/Hfl.
1370 UPTRKE
250 500 750 1000 1250
flCCUMULRTlVE MRNURE flPPLICHTION,
1971 UPTflKE
1.6-r
0.0-
0 125 250 375 500 625
flCCUKULflTIVE MRNURE RPPLICOT10N, MT/Hfi.
0.0
0 250 500 750 1000 1250
RCCUMULflTlVE KRNURE RPPLiCRTICN. MT/Hfl
Figure 32. Corn forage yield and manganese uptake as affected by accumulative yearly applications
of beef feedlot manure (dry weights) that began in 1969.
-------
03
60-
CE
X
50-
o
_)
UJ
o
ff
o
"-30^
z
cc
o
20
1971 YIELD
n ?? 44 63 88 1
Accumulative Lagoon Water, CM
1971 UPTRKE
lO-
cs
7 e-
-------
The two highest yearly manure treatments were the only feedlot waste
treatments which increased DTPA-extractable Cu. Cores from plots re-
ceiving the residual manure and lagoon water treatments had levels of
DTPA Cu that were either similar to or lower than levels measured in
control plot cores (Figure 34).
Copper uptake by corn forage and Cu content in corn forage was not
affected by the yearly or residual manure treatments. A linear decrease
in Cu content of corn leaf tissue occurred in 1971, the only year that
yearly manure treatments influenced this measurement. Corn leaf content
of Cu had opposite quadratic effects due to residual manure treatment in
1971 and 1972: in 1971 Cu content was maximized by the intermediate
residual treatments, while in 1972 these same treatments minimized Cu
content in corn leaves. An explanation for these opposing trends is not
obvious. Uptake of Cu by corn forage grown on plots receiving the
lagoon water treatments followed trends that were similar to yield
trends: linear increase in 1970 and quadratic (maximization at the
intermediate rates) in 1971 and 1972. A quadratic trend in Cu content
of corn forage due to lagoon water was found in 1971 only (Table 18).
The soil and plant Cu data showed little consistent response to appli-
cation of beef feedlot wastes.
89
-------
o—0 CONTROL
£30 NI/Mfl.
181
.15 0.51 O.C3 0.73 ' 0.81 " 0.
90
LRGOON WflTPR
»—n COMiriOL
o CH/rtnn
15
23
* W3
D.2
O.V
O.Ci 0.8
CU. PPM
1.0
I.
Figure 34. DTPA extractable Cu as affected by depth and applications
of beef feedlot wastes.
90
-------
SECTION XI
DENITRIFICATION STUDY
GENERAL
Since denitriflcation could be significantly affecting the N balance
of the neutral to basic soil on the manure disposal plots, four plots
were selected for more detailed study in the summers of 1972 and 1973.
In these plots, soil chemical and atmospheric conditions that affect
denitrification or suggest its presence were measured.
METHODS AND PROCEDURES
The denitrification study was conducted on four plots in the manure
disposal study area which has been described in Section IX of this
report. By the summer of 1973, the average annual treatments were 0,
58, 306, and 687 MT/ha. of dry manure.
Soil cores collected to a depth of three meters in the fall of 1969
before manure applications and in the fall of 1971 after two years of
treatments were analyzed in 10-cm increments for total N to one meter
(not to include NOa-N) by micro-kjeldahl digestion with sulfuric acid
and subsequent steam distillation (Keeney and Bremner^7) and for NO^-N
to three meters by steam distillation. One-meter soil cores taken in
the fall of 1970 and 1972 after one and three manure applications,
respectively, were analyzed in 10-cm increments for organic C using a
LECO 70-Second Analyzer(Belo72 and Tabatobai and Bremner73) to obtain C
and subtracting the carbonate-C obtained by acid neutralization (Black74),
Soil-atmosphere-access tubes were installed in mid-July of 1972 and 1973
at seven depths (5-10, 10-20, 20-30, 30-40, 40-60, 60-80, and 80-100 cm),
each depth being replicated four times in each plot. The tubes were
built and installed so that the gas within the tube would come to equi-
librium with the gas in the soil depth being sampled (Figure 35). In
early September of 1972 and 1973, 10-ml gas samples were removed by
syringe from the tubes and transferred to 15-ml glass bottles that had
been evacuated by a hand vacuum pump to 38.1 cm of mercury. The samples
were analyzed for Na, 02, COa, CHi^, and N20 using a Carle Model 8000 gas
chromatograph with Porapak-Q (first) and molecular sieve (second)
columns installed in series. Flow rate was 25 milliliters per minute
91
-------
RUBBER SEPTA
SOIL-
SOIL SURFACE
.1.91cm
.38cm
RIGID PLASTIC PIPE
SOIL^ DEPTH
BEING SAMPLED
Figure 35. Soil-atmosphere-across tube design.
92
-------
(ml/min) and oven temperature was 55° C. It was assumed that no gases
other than the above five would be present in significant quantities.
Area normalization with correction factors for the relative sensitivity
of the machine for each gas was used for calculation of percentage
composition (McNair and Bonelli75). The time between collection and
analysis was approximately six months for the 1972 samples and one month
for the 1973 samples.
In 1972, one-meter soil cores were taken in May, June, July, and Sep-
tember at four locations in each of the four plots. The May sampling
was made approximately two weeks after planting and the later samplings
were made from 7-14 days after 10-cm irrigations. The cores were divi-
ded into seven depth increments, stored in plastic bags, and frozen in
the field with dry ice. After crushing the frozen soil samples to
obtain a representative sample, the soil was analyzed for NH^-N and
NC>3-N by steam distillation (Keeney and Bremner67), for NOJ-N by the
Greiss-llosvay method (Black74), and for gravimetric water. In 1973,
soil solution samples were obtained by porous cups at six depths to one
meter at four locations in each plot. Vacuum was applied to the cups
on August 10, one day after a 10-cm irrigation, and on August 24, one
day after an 8-cm rain. Vacuum was maintained until water samples were
collected the next day and refrigerated. The solution samples were
analyzed for NH*-N and NO^-N by steam distillation (Keeney and Bremner67),
for NOa-N by the Greiss-llosvay method (Black74), and, after filtering,
for Fe and Mn by atomic absorption spectrophotometry.
RESULTS AND DISCUSSION
Total Nitrogen and Organic Carbon
Nitrogen balance calculations based on the total N and NO^-N analysis
of the fall 1970 and 1971 soil cores are given in Table 19. It can be
seen that significant amounts of N cannot be accounted for by the
measurements used. The plots receiving the two lowest manure treat-
ments lost more nitrogen from the fall of 1969 to the fall of 1971 than
was added in the manure during that period, indicating that the manure
had caused disappearance of native N. Of the plots receiving manure,
the ones receiving the heaviest manure treatments had the least amount
of unaccountable N. In work we reported earlier (Murphy et al.76), soluble
salt accumulations in the soil were thought to be responsible for the
decreased growth of corn by increasing the osmotic potential of the
soil solution. This negative growth factor could have similarly
affected the functioning of denitrifying organisms and lowered net N
loss from plots receiving the large tonnages of manure.
Total N concentrations in the 1971 soil cores increased to a depth of
50 cm under plots receiving 522 MT/ha./yr and increased to a depth of
10 cm under plots receiving 298 MT/ha./yr (Figure 36). The lower
treatments did not appreciably change total N content at any depth.
93
-------
Table 19. NITROGEN BALANCE CALCULATIONS LN PLOTS THAT
HAD RECEIVED APPLICATIONS OF BEEF FEEDLOT MANURE (DRY MT/ha.)
Accumulative manure applied
Control
58
85
8
5958
1043
irr/ha.
Fall 1969
Average kjeldahl % N-lm depth0 0.0658
kg in 1 ha.-ma 9212.0
Average ppm NOf-N - 3m depth 1.0
kg in 3 ha.-na 42.0
Total N - kg/ha. b 9250.0
Fall 1971
Average kjeldahl % N-lm depth° 0.0633
kg in 1 ha.-ma 8860.0
Average ppm N'O^-N - 3m depth 1.1
kg in 3 ha.-m4 8910.0
Total N difference - kg/ha. d -340.0
N added in manure - kg/ha. 0.0
N removed by corn - kg/ha. 204.0
Unaccounted for Ne 136.0
a The bulk density of the soil was 1.4 g/cmj
b It was assumed that there was no change in
0.0858
12010.0
1.5
63.0
12070.0
0.0746
10440.0
1.9
10520.0
-1550.0
580.0
200.0
1930.0
.
kjeldahl N
c The soil samples were contaminated with Nrf£-N during
distillable Nh~t-N was subtracted from the
d Total N in 1971 minus total X in 1969.
e Unaccounted for « « N added in manure - N
f Data from one control plot.
g Average of two plots.
kjeldahl N
0
13500
2
84
13580
0
11130
2
11250
-2330
850
353
2830
below
.0964
.0
.0
.0
.0
.0795
.0
.8
.0
.0
.0
.0
.0
1 m.
cold storage
and the
removed by com -
0
11520
1
71
11590
0
10930
6
11210
-380
2020
384
2020
.0823
.0
.7
,0
.0
.0781
.0
.7
.0
.0
.0
,0
.0
To correct
difference
Total
0.
9530.
2.
97.
9630.
0.
10490.
7.
10780.
+1150.
3720.
358.
2210.
0681
0
3
0
0
0749
0
0
0
0
0
0
0
0.
10370.
1.
59.
10430.
0.
13730.
13.
14280.
+3850.
5950.
364.
1740.
0741
0
4
0
0
0981
0
2
0
0
0
0
0
for this contamination,
0.
10680.
1.
63.
10740.
0.
19840.
9.
20240.
+9500.
10430.
235.
700.
0763
0
5
0
0
1417
0
5
0
0
0
0
0
steam
reported here.
N difference.
-------
TOTRL N. 1971
o
o
o_
UJ
o
CONTROL
29 MT/HA./YR
43
101
186
298
522
10o°oo
0,08 0/16 0.24 0.32
TOTRL N, PERCENT
0.40
Figure 36. Total N (dry weight basis) in soil cores as affected by
depth and two years of beef feedlot manure applicntions.
95
-------
Organic carbon increased relative to the control at the 10-cm depth in
all three manured plots in 1970 and 1972 (Figure 37). Movement of C to
the 50-cm depth was evident in the 1972 soil sampling from the plot that
received 687 MT/ha./yr. Some of this increased C would be available for
oxidation in denitrification reactions.
Soil Atmosphere
Analyses for N2, 02, C02, CHU, and N20 in the atmospheric samples taken
in late summer of 1972 and 1973 were averaged over the four replications
at each depth and are presented in Figures 38-41. No trend due to
treatment is evident in the 1972 N2 data, but the 1973 data do show
lower percentages of N2 at all depths beneath the plot that received 687
MT/ha./yr of manure (Figure 38). This lower N2 percentage was probably
due to higher levels of C02 and CH^ found in these samples (Figures 40
and 41), which would have displaced N2 and lowered its relative concen-
tration. Increased levels of N2 would be expected if denitrification
had been occuring, but production of N2 by denitrifying organisms could
have been overshadowed by increased production of C02 and CH^.
Lower percentages of 02 were found at several depths beneath the plots
receiving 687 MT/ha./yr of manure at the 1972 sampling and beneath plots
receiving 306 and 687 MT/ha./yr at the 1973 sampling. Lower 02 percent-
ages could have been due to removal of 02 for organic matter oxidation
or increased concentrations of C02 and CH^ which could have lowered the
relative concentrations of 02.
At the 1972 sampling, C02 percentages were higher in the surface 40 cm
under the plots receiving 687 MT/ha./yr, and at the 1973 sampling, C02
was increased at all sampling depths beneath plots receiving 306 and 687
MT/ha./yr (Figure 40). Higher C02 concentrations reflect greater res-
piration of soil organisms resulting from the addition of organic matter
in the manure. More C02 was found throughout the surface meter even
though organic C was not increased appreciably below 50 cm (Figure 37).
This could be explained by diffusion of C02 downward.
No CH2 or N20 was found in the 1972 gas samples. Analysis of samples
taken in 1973 beneath the plot receiving 687 MT/ha./yr of manure did
show significant concentrations of CH^ at all depths except the one
closest to the soil surface (Figure 41) . No CH,, was found in samples
from three plots. Methane does indicate that anaerobic conditions
existed beneath the plot receiving the heaviest manure treatment.
Nitrous oxide in the 1973 samples was found in the lower portions of the
surface meter under plots receiving the two heaviest manure treatments,
but not under the control plot nor the lightest manured plot (Figure
41). Since N20 is an end product of denitrification, its presence
indicates that those reactions did occur.
The soil atmosphere sampling technique was adequate for monitoring the
appearance or disappearance of the gases measured. The large, variable
96
-------
ORGflNIC CflRBON, 1970
o-
25-
z-- 50-
o_
UJ
75-
©—© CONTROL
x—x 58 MT/HA./YR
o—e- 306 MT/HA./YR
* * 687 MT/HA. /YR
100-1 i . 1 . 1 • 1—
0.0 0.4 0.8 1.2 1.6
CflRBON, PERCENT
ORGRNIC CflRBON, 1972
0
2 0
©—0 CONTROL
x—x 58 MT/HA./YR
30GMT/HA./YR
* * G87MT/HA./YR
'0 0 017 l.U 2; I 2.8
CflRBON, PERCENT
Figure 37. Organic C (dry weight basis) in soil cores as affected by
depth and yearly beef feedlot manure applications.
97
-------
0
25-
x 50-
Q_
UJ
Q
75-
100
x~ 50
o_
UJ
Q
100
NITROGEN, 1972
O—© CONTROL ,
*—x 58 MT/HA./YR
306 MT/HA./YR
587 MT/HA./YR
78
80
NITROGEN, PERCENT
NITROGEN, 1973
76 78
NITROGEN, PERCENT
Figure 38. Nitrogen gas in soil atmosphere as affected by depth and
yearly beef feed Lot manure applications.
-------
25-
o_
LJ
Q
75-
10DJ
OXYGEN, 1972
©—e> CONTROL
x—x 58 MT/HA./YR
o—e. 306 m/HA./YR
*—« 687 MT/HA./YR
TU
0-
25-
x 50-
o_
UJ
Q
75i
100
16
18
OXYGEN.
20
PERCENT
OXYGEN, 1973
i * i
o—o CONTROL
x—x 58 W/HA./YR
o—e. SOB -;T/HA,/YR
x—x 687 rtr/HA./YR
14 16 18 20
OXYGEN, PERCENT
22
Figure 39. Oxygen gns In noil atmusptieru .-IH .-jfroi-ted by depth ;ind
yearly becif feed lot manure ap|>l l.cat Jons.
99
-------
s:
o
Q-
UJ
O
25-
50-
75-
100
CflRBON DIOXIDE, 1972
> > i * . i
o
Q_
UJ
25-
50-
75-
100
e—e> CONTROL
x—x 58 i MT/HA./YR
<>—* 306 MT/HA./YR
x—* 687 MT/HA./YR
0 1 2 3 U
CflRBON DIOXIDE, PERCENT
CflRBON DIOXIDE, 1973
T ' 6 ' "T
DIOXIDE, PERCENT
10
Figure 40. Carbo:i dioxide in soil atmosphere as Defected by de])Lii
and yearly beef feedlot manure applications.
100
-------
METHRNE. PERCENT
Q_
LU
100
07000 0.012 0.02U ' 0.036 ' 0.048 ' 0.060
NITROUS OXIDE, PERCENT
Figure 41. Nitrous oxide and methane in soil atmosphere as affected by depth and yearly beef f?ed-
lot manure applications.
-------
volume of the access tube makes quantification difficult, but profile
distributions of relative concentrations were successfully measured.
1972 and 1973 Soil Solution Analyses
Analyses of the 1972 and 1973 soil solution samples were averaged over
all sampling dates and are presented in Figures 42-44. The results of
the 1972 and 1973 analyses are expressed as parts per million (ppm) in
air dry soil and ppm in soil solution, respectively. When comparing
the relative magnitudes of the 1972 and 1973 NOs-N and NO-j-N data, the
1972 data should be multiplied by 3 to correct the concentration effect
that would occur if the dry soil were wetted and the solution analyzed.
Relative to the control plot, NO^-N concentrations were greater through-
out the entire surface meter in soil cores taken in 1972 from the three
manured plots (Figure 42). The magnitude of NOa-N concentrations were
much greater in the two plots receiving the heaviest treatment, indi-
cating large amounts of N were being nitrified into NOj-N and leached
downward. Increased NOJ-N was found in 1972 only in the surface 25 cm
of plots receiving the two heaviest manure treatments^ An intermediate
product of both nitrification and denitrification, N02-N indicates at
least one of the above reactions was occuring in the surface 25 cm.
Nff*"-N was also found in higher concentrations in cores taken from the
two plots receiving the highest manure rates (Figure 42), reflecting
ammonification of nitrogenous compounds added in the manure.
Increased NOg-N concentration were found generally at 50- to 100-cm
depths in soil-solution samples taken from the manured plots in 1973.
NCU-N was only found in the soil solution beneath the two heaviest
manured plots, the concentrations under the plot receiving 687 MT/ha./yr
being highest from 50 to 100 cm. The NHf-N concentrations in the soil
solution samples showed no trend due to treatment or depth. The values
were generally high beneath all plots including the control (Figure 43).
High NOg-N concentrations were found in the summer samplings of both
years. The 1972 soil samples were collected at least one week after
irrigations, while the 1973 soil solution samples were taken when the
soil was wet from an irrigation and a rain. Later sampling dates in
1972 (relative to wet soil conditions), allowing re-aeration of the soil
and nitrification reactions to resume, indicated why N03-N concentrations
were found uniformly higher throughout the surface meter in 1972. The
1973 soil solution samples were collected when the soil was still wet
and probably oxygen dificient, conditions conducive to denitrification.
Entrance of NO~-N into denitrification reactions caused generally lower
concentrations of NOg-N in the surface 50 cm than between 50 and 100 cm
in 1973.
Iron in the soil solution samples was higher under the three manured
plots than under the control plots. The magnitude of Fe concentrations
were greater with the heavier applications (Figure 44). Manganese
102
-------
o
UJ
as-
r:
u
x 50->
0.
UJ
o
100-
25-
50-
o.
UJ
75
100
N1TRRTE-N. 1972
O—O CONTROL
58 ,KT/t«./YR
306 MT/HA./YR
687 KT/HA./YR
20
80
^o 60
NITRflTE-N, PPM
RMMONIUM-N, 1972
CONTROL
58 MT/HA./yR
306 MT/HA./YR
687 MT/HA./YR
' 4 ' 6
BMMONlUn-N. PPK
25<
i 50*
o.
UJ
o
100
10
75-
IOC
0
NITRITE-N,
0—0 CONTROL
58 MT/HA./YR
306 HT/HA./YR
687 HT/HA./YR
0.5 1.0 1.5 2.0
NITR1TE-N, PPM
2.5
Figure 42. Nitrate-N, nitrite-N, and ammoniuia-N (dry weight basis) in soil cores as affected by
depth and yearly beef feedlot manure applications.
-------
100
100
NITRRTE-N., 1973.
NITRITE-N,, 1973.
60 90
N1TRHTE-N. PPM
RMMONIUM-N, 1973
NITBITE-N. PPM
58 MT/Hft./YR
/HA./Y
B87 MT/HA./YR
20 40 60
BMMONIUM-N. PPH
100
Figure 43. Nitrate-N, nitrite-N, and aromonium-N in soil solution as affected by depth and yearly
applications of beef feedlot manure.
-------
MRNGRNESE, 1973
©—e> CONTROL
x—x 58 MT/HA./YR
306 MT/HA./YR
*—* 687 MT/HA./YR
O.U
o:s 1.2
MRNGRNESE, PPM
25<
o
£ 50<
0_
UJ
O
75
/
10o°oo
IRON, 1973
e—e> CONTROL
x—x .58 MT/HA./YR
« o 306 MT/HA./YR
x—x 687 MT/HA./YR
0.08 0.16 0.24
IRON. PPM
0.32 0.40
Figure 44. Iron and manganese in soil solution as affected by depth
and yearly applications of beef feedlot manure.
105
-------
concentrations in soil solution were increased by the two heaviest
manure treatments to levels higher than those of Fe (Figure 44). The
687 Mt/ha./yr treatment increased Mn throughout the surface meter. Meek
_et al. found that Mn and, to a lesser extent, Fe solution concentra-
tions were increased when an organic matter-amended soil was flooded.
They attributed the increased solubility of these elements to chemical
reduction in the anaerobic conditions measured in the soil. Fe and Mn
data from this study were indirect evidence for the presence of anaero-
bic conditions necessary for denitrification.
106
-------
SECTION XII
RUNOFF FROM LAND APPLICATION OF FEEDLOT WASTES
GENERAL
Success in disposing of feedlot wastes onto cropland depends upon the
quality of the surface runoff waters. Characteristics of runoff from
irrigations and rainfall were measured on the plots used for disposal of
feedlot runoff and feedlot manure.
METHODS AND PROCEDURES
The waste disposal plots have been described in Sections VIII and IX of
this report.
During the corn growing season of 1970 and 1971, runoff from the three
center furrows of each plot was directed through an orifice in a plate
of sheet metal. A sample bottle was connected by a 0.63-cm diameter
plastic tube to a 0.31-cm diameter orifice drilled in the sheet metal
plate. A second plastic tube vented the sample bottle to the atmosphere
at the top of the orifice plate. As runoff occurred, the sample bottle
filled from the first runoff. When no further flow could enter, the
sample was retained for later analysis in the laboratory.
During the 1973 irrigation season, equipment was installed to measure
and sample rainfall runoff from three plots receiving annual applica-
tions of manure. Runoff from the center three furrows of each plot was
directed through a 2.54-cm trapezoidal flume. Flow was measured by a
water level recorder activated by a float. The runoff was sampled every
5 minutes during the runoff event by an automatic vacuum sampler. Grab
samples of runoff from irrigations with well water were taken from these
three plots and two additional replications of the three treatments.
Table 20 gives annual manure treatments to the disposal plots.
107
-------
Table 20. ANNUAL MANURE APPLICATIONS TO DISPOSAL PLOTS'
(MT/ha.)
Year
Plot
1969
1970
1971
1972
M-l
M-4
M-9
0
137
470
0
65
435
0
152
692
0
72
457
Dry Weights.
Samples were collected and refrigerated after each runoff event. They
were packed in ice during transport to Manhattan and refrigerated until
analyzed.
Chemical oxygen demand and five-day biochemical oxygen demand
were determined according to methods listed in Standard Methods.65
Total N determinations were made using the micro-kj eldahl method de-
scribed by Carter.77 Ammonia-nitrogen was determined by the procedure
described in Standard Methods65 using the direct nesslerization method,
and NO^-N determinations were made with a standard Each DR-EL direct
reading engineers' laboratory kit. Total P determinations were run as
described in Standard Methods65 using method C and exercising the auto-
clave option. The Millipore vacuum filter technique was used for total
suspended solids (SS) determinations. Turbidity determinations, expressed
in Jackson Turbidity Units (JTU), were made with a Hach Laboratory
Turbidimeter Model 1860, and EC was determined using a Lab-Line Lectro
Mho Meter Model MC-1, Mark IV.
RESULTS AND DISCUSSION
Quality of Initial Runoff
During 1970 and 1971, samples were initial runoff of a runoff event from
the waste disposal plots. The quality of irrigation runoff from the
manured plots was relatively good with COD concentrations of 10 to 50
mg/£, total N ranging from 5 to 25 mg/£, and P approximately 1 mg/£.
Runoff from rainfall, however, carried a higher pollutant load. COD
concentrations ranged from 100 to 400 mg/£ with a trend for higher
concentrations from the heaviest manure treatments, total N ranged from
14 to 29 mg/£, and P ranged from 3 to 5 mg/£.
Irrigation runoff from disposal plots receiving annual applications of
feedlot runoff had COD concentrations of 40 to 90 mg/£ and total N
ranging from 22 to 27 mg/£. Runoff from rainfall had CODs ranging from
100 to 600 mg/£ and total N ranging from 15 to 25 mg/£.
108
-------
Table 21. CHARACTERISTICS OF RAINFALL RUNOFF
Plot
M-9
M-l
M-4
M-9
M-l
M-9
COD BOD5 SS
mg/fc tng/X. mg/S,
range mean range mean range
July 20,
118-716 473 4.0-13.4 8.8 144-1,156
September 2
101-601 232 9.5-22.5 L6.1 172- 664
83-201 120 4.7- 6.4 5.4 328- 668
September 12
117-459 180 7.6-8.1 7.8 168- 394
September 16
66-122 82 4-6- 8.6 6.4 171- 564
161-241 174 5.4-9.2 7.0 192- 852
mean
1973
477
, 1973
420
479
, 1973
276
, 1973
242
3.2
Turbidity Conductivity
JTU mmhos / cm
range mean range mean
29-340 164 0.53-4.70 2.96
61-155 98 0.20 0.20
55-190 118 0.17-0.19 0.18
32-300 122 0.53-0.68 0.57
120-185 134 0.10-0.13 0.12
96-235 122 0.70-0.94 0.88
-------
Table 22. CHARACTERISTICS OF RAINFALL RUNOFF
Plot Tot*J N
mg/£
range mean
fc-9 5.8-35.5 22.7
M-l 1.9- 6.0 4.6
M-4 2.9- 5.0 3.9
M-9 5.0-33.8 7.5
Mr-1 0.9- 2.9 2.5
Ii-9 7.6- 8.2 7.8
N03-N
mg/Jl
range mean
July 30,
3.7-97.0 61.6
September 2
0.0- 0.8 0.3
0.3- 0.8 0.3
September 12
3.5-37.0 6.4
September 16
0.8- 1.8 1.0
9.3-10.3 9.9
NH -H
fflg/i
range mean
1973
1.1-4.0 2.7
, 1973
1.0-1.8 1.0
0.4-1.3 1.2
, 1973
1.0-2.8 1.3
, 1974
0.0-0.7 0.2
0.9-1.6 1.0
Total
mg/fc
range
6.26-19.18
0.85- 3.59
0.85- 2.22
3.43- 5.42
0.98- 1.15
3.45- 3.82
P
mean
13.97
1.78
1.59
4.50
1.08
3.68
-------
The higher concentration of COD in the rainfall runoff can be attributed
to erosion due to impact of the falling raindrops onto the soil. The
entire plot area contributed during rainfall while during irrigations
only the weathered area in the furrows contributed to runoff.
Quality of Runoff from Manured Plots, 1973
The runoff samplers were installed on June 5, 1973, and operated through
September 17, 1973. During this time, samples were collected from four
irrigations with well water and four of the five runoff-producing
rainfall events. Due to mechanical difficulties with the automatic
samplers, samples were not collected from all three plots during each
rainfall-runoff event.
Tables 21 and 22 give dates and characteristics of runoff from rainfall
The rainfall event on July 30 was three weeks after the corn was furrowed
for irrigation and 15 days after the first irrigation. The storm was of
high intensity and came when the corn plants were about one-third of
their mature size. Runoff in September occurred under ideal conditions
for minimum pollution concentrations as the crop was nearing maturity
and the soil had not been cultivated for several months.
As samples were not collected from each treatment during each runoff
event, it was impossible to directly evaluate the effects of manure
treatment on runoff quality. COD was chosen as the basis for comparing
the various pollutional parameters because it was highly correlated with
other pollutional parameters for feedlot runoff (Section V of this
report). Table 23 gives selected mean COD:pollutional parameter ratios
for individual runoff events.
Table 23. MEAN COD:POLLUTION PARAMETER RATIO
Plot
I M-9
II M-l
II M-4
III M-9
IV M-l
IV M-9
COD: BOD R
54:1
14:1
22:1
23:1
13:1
25:1
COD: Total N
6:1
47:1
29:1
13:1
23:1
10:1
COD: Total P
34:1
130:1
75:1
40:1
76:1
47:1
COD : SS
1:1
1:2
1:4
:2
1:3
:2
BOD, was consistently below 10 mg/£ (Table 21) indicating that the BOD5
load applied by the waste was assimilated by the microorganisms in the
soil. Therefore, the BOD5 data indicate a background level caused by
material always present in the soil and were not influenced by waste
111
-------
application the previous October. The COD was not completely assimila-
ted, so higher waste applications result in higher COD losses. This is
shown by the ratios (Table 23) where less COD was given off per unit of
from the lower pollution potential plots, M-l and M-4.
Table 22 shows that for the check plot, M-l, and the lower waste appli-
cation, M-4, most of the N and P was assimilated by the soil leaving
only a small residual to react with the elements and leave in runoff.
Of the heavy waste application, M-9, only a portion of the total N and P
could be assimilated by the soil leaving a larger residual to react with
the elements and remain in runoff. Since soil has a limited capacity for
COD reduction, as waste application increased, so did residual which can
be acted upon and lost. The ratios (Table 23) show this by the fact
that more COD per unit of total N and P was given off on the lower
pollution-potential plots.
CODrSS ratios in Table 23 show no trend. There is sufficient cause to
state that a significant portion of the COD was soluble and not related
to suspended solids. It appears that the concentration of suspended
solids in the runoff is based upon storm intensity and soil conditions.
Tables 24 and 25 give dates and characteristics of irrigation runoff.
The irrigation on June 15 was about one week after the plots were
furrowed and light rainfall fell during the later stages of the irriga-
tion. These factors account for the higher pollutant concentrations for
this irrigation.
As for the rainfall runoff events, the irrigation runoff events and
their associated pollutional parameters were compared on a COD basis.
No trends could be defined when the mean ratios were examined.
112
-------
Table 24. CHARACTERISTICS OF IRRIGATION RUNOFF
Plot
COD
mg/A
range
M-l
M-4
M-9
23-
18-
94
34
68-160
mean
50
25
110
BOD
mg/£
mean
First
4.80
5.36
5.00
SS
mg/Jl
mean
irrigation -
996
302
62
Second Irrigation
M-l
M-4
M-9
M-l
M-4
M-9
M-l
M-4
M-9
10-
8-
27-
3-
2-
24-
6-
8-
39
16
64
6
15
72
8
18
29-139
26
12
46
5
8
41
7
12
78
4.50
2.14
5.06
Third
6.26
3.24
4.95
Fourth
3.45
2.50
3.10
380
50
46
irrigation -
36
8
180
irrigation -
55
195
634
Turbidity
JTU
range
June 15,
50-260
39- 78
11-120
- July 2,
6-100
4- 24
3- 22
August 6,
2- 12
1- 4
2-115
August 20
7- 8
15- 36
7-135
mean
1973
132
55
52
1973
55
14
11
1973
7
2
51
, 1973
8
25
52
Conductivity
nnnhos/cm
range
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
58-0.
61-0.
84-1.
54-0.
56-0.
63-0.
50-0.
49-0.
60-0.
55-0.
51-0.
64-0.
62
64
10
61
60
82
63
61
73
59
60
88
mean
0.61
0.63
0.95
0.57
0.58
0.69
0.57
0.55
0.64
0.57
0.56
0.74
-------
Table 25. CHARACTERISTICS OF IRRIGATION RUNOFF
Plot
M-l
M-4
M-9
M-l
M-4
M-9
M-l
M-4
M-9
M-l
M-4
M-9
Total N
mg/X.
range mean
0.4-3.3 1.5
0.4-1.2 0.9
1.7-7.2 4.6
0.4-1.6 0.9
0.5-0.8 0.6
1.1-2.2 1.8
0.5
0.5
1.3
0.4
0.1
1.9
NO,-N
mgV*
range mean
First irrigation -
1.0-3.0
5.0-7.0
2.0-4.0
Second irrigation -
1.8-2.8
2.0-2.2
2.8-3.8
Third irrigation -
3.5-3.8
3.9-4.4
3.5-4.2
Fourth irrigation -
4.0-4.6
3.9-4.5
3.4-5.1
June 15
1.7
6.0
2.7
July 2
2.2
2.1
3.2
August
3.7
4.1
3.8
August
4.3
4.3
4.4
NH^-N
mg/Jl
mean
, 1973
0.0
0.0
0.3
, 1973
0.1
trace
0.3
6, 1973
1.3
0.0
0.5
20, 1973
0.0
0.0
0.6
Total
mg/i
range
0.13-0.44
0.24-0.79
3.46-5.22
0.0 -0.34
0.11-0.36
0.85-1.05
0.02-0.35
0.0 -0.16
0.79-1.90
0.04-0.11
0.06-0.24
2.09-5.84
P
I
mean
0.29
0.47
4.53
0.15
0.27
0.92
0.15
0.09
1.51
0.08
0.16
3.37
-------
SECTION XIII
MOVEMENT OF WATER INTO SOIL RECEIVING FEEDLOT MANURE
GENERAL
Incorporation of feedlot manure into soil will alter the soil's chemical
and physical composition. Changes in soil composition will most likely
change water intake characteristics. The effect of manure loading rate
on the basic intake rate of irrigation water into the soil was evaluated.
METHODS AND PROCEDURES
The study was conducted on the manure disposal area described in Section
IX of this report. Corn was irrigated with well water in furrows on
0.76-m spacing in 1970, 1971, and 1972 and 1.52-m spacing in 1973.
Basic intake rates were determined from inflow and outflow measurements
during each irrigation.
During each irrigation, water was delivered to the furrows for 30 to 48
hours. A basic intake rate was assumed after the runoff hydrograph
leveled off, 6 to 12 hours after runoff began. Inflow and runoff were
measured for three furrows in 1970, 1971, and 1972 and two furrows in
1973 of each plot a minimum of three times during the basic intake
period. Intake rates were taken as the difference between inflow and
outflow and were calculated assuming the entire soil surface was covered
with water. The basic intake rate for each plot during each irrigation
was taken as the average of the calculated basic intake rates. Stritz-
ke78 gives further details of inflow and outflow measurements and intake
rate calculations.
RESULTS AND DISCUSSION
Table 26 gives basic intake rates in centimeters per hour (cm/hr), dates
of irrigations, and dry manure application rates. As furrows were on
1.52-meter spacing in 1973 and 0.76-meter spacing the other years, basic
intake rates for 1973 cannot be compared directly with those for the
other years.
115
-------
Table 26. MANURE APPLICATION KATE AND BASIC INTAKE RATE
Plot
11
12
13
14
15
16
17
18
19
10
21
22
23
24
25
26
27
28
29
20
31
32
33
34
35
36
37
38
39
30
Manure
MT/ha.
1969
137
159
455
0
470
63
269
327
215
20
414
141
72
0
54
20
123
589
372
302
233
609
204
506
0
76
226
175
47
38
Baaic Intake Rate
cm/hr
6/25/70
0.274
0.175
0.401
...
0.127
0.302
0.086
0.218
0.066
0.211
0.163
0.066
0.183
0.135
0.084
0.104
0.193
0.109
0.061
0.244
0.170
7/09/70
0.157
0.109
0.061
0.193
0.114
0.208
0.147
—
0.145
0.122
0.384
0.109
0.165
0.089
0.107
0.130
0.043
0.147
0.170
0.076
_ —
0.122
0.183
0.064
0.071
0.259
0.061
7/23/70
0.224
0.097
0.048
0.221
0.175
0.310
0.097
0.178
—
0.124
0.122
0.366
0.074
0.168
0.071
0.147
0.163
0.018
0.175
0.071
0.046
- —
0.056
0.127
0.140
0.058
0.079
0.244
0.099
8/06/70
0.399
0.170
0.046
0.282
0.206
0.394
0.140
0.213
—
0.178
0.124
0.373
0.030
0.191
0.079
0.145
0.178
0.165
0.168
0.023
0.102
0.119
0.145
0.114
0.097
0.442
0.124
Manure
MT/ha.
1970
65
184
0
0
435
31
0
296
0
34
558
112
128
0
29
18
0
0
0
444
0
569
0
0
0
128
343
226
16
40
Basic Intake Rate
cn/hr
4/06/71
0.325
0.282
0.130
0.175
0.196
0.127
0.160
0.081
0.269
0.056
0.213
0.335
0.023
0.135
0.033
0.003
0.018
0.262
0.269
0.282
0.015
0.312
0.023
0.109
0.226
0.005
_-,_
0.089
0.036
7/13/71
0.257
0.140
0.246
0.170
0.086
0.191
0.140
0.107
0.051
0.142
0.363
0.472
0.211
0.241
0.175
0.376
0.157
0.279
0.287
0.432
0.036
0.302
0.185
0.152
0.180
0.384
0.269
0.272
7/27/71
0.206
0.168
0.211
0.572
0.086
0.097
0.056
0.157
0.028
0.119
0.069
0.312
0.063
0.061
0.005
0.135
0.081
0.114
0.201
0.335
0.010
0.236
0.127
0.086
0.066
0.137
-__
0.155
0.462
8/10/71
0.150
0.135
0.208
0.404
0.160
0.140
0.058
0.058
0.030
0.135
0.142
0.345
0.015
0.030
0.003
0.076
0.043
0.119
0.175
0.208
0.008
0.208
0.089
0.155
O.O36
0.109
_—
0.056
0,066
-------
Table 26 (Continued). MANURE APPLICATION RATE AND BASIC INTAKE RATE
Plot
11
12
13
14
15
16
17
18
19
10
21
22
23
24
25
26
27
28
29
20
31
32
33
34
35
36
37
38
39
30
Manure
MT/ha.
1971
152
188
0
0
692
76
0
439
0
31
423
202
110
0
78
34
0
0
0
390
0
977
0
0
0
242
340
213
31
103
Basic
7/20/72
0.302
0.284
0.409
0.427
0.404
0.274
0.297
0.282
0.434
0.645
0.386
0.315
0.071
0.442
0.196
0.191
0.236
0.325
0.025
0.145
0.282
0.221
0.208
0.183
0.216
Intake
cn/hr
8/02/72
0.371
0.282
0.198
0.201
0.180
0.130
0.157
0.150
0.290
0.259
0.257
0.185
0.030
0.008
0.030
0.038
0.193
0.038
0.058
0.076
0.132
0.081
0.130
0.025
0.211
— -
Rate
8/16/72
0.353
0.251
0.147
0.198
0.264
0.175
0.155
0.173
0.170
0.175
0.297
0.190
0.048
0.104
0.081
0.061
0.094
0.135
0.226
0.104
0.343
0.074
0.122
0.140
0.132
0.155
0.094
0.104
0.193
0.089
Manure
1972
72
157
0
0
457
83
0
202
0
29
654
159
108
0
67
56
0
0
0
184
0
591
0
0
0
148
314
179
29
52
Basic
7/02/73
_- .-
0.091
0.063
0.033
0.132
0.150
0.104
0.145
0.157
0.076
0.119
0.013
0.127
0.157
0.155
0.175
0.226
0.114
0.069
0.170
0.305
0.028
0.046
0.168
0.348
0.041
0.005
0.378
Intake
ctn/hr
8/06/73
— «
0.081
0.046
0.003
0.028
0.094
0.063
0.071
0.114
0.155
0.168
0.127
0.089
0.097
0.074
0.089
0.122
0.081
0.058
0.152
0.081
0.142
0.107
0.064
0.132
0.112
0.175
0.152
0.117
Rate
8/20/73
___
0.048
0.048
0.023
0.053
0.066
0.091
0.061
0.234
0.155
0.173
0.066
0.127
0.119
0.145
0.086
0.155
0.137
0.137
0.091
0,104
0.109
0.124
0.069
0.155
0.058
0.135
0.150
0.173
-------
Basic intake rates for the three replicated blocks were pooled and
analyzed by multiple regression methods. The following equations were
developed:
An I?0 = -1.85 - 6.32 x i(f4 M6g + 3.66 * 10~7 M2^
-3.42 v 10~9 M3g , R2 = 0.16 (8)
In I?1 = -2.50 + 8.58 x 1Q~3 M6g + 7.39 x 10~6 M2g
-3.72 x 10~8 M3 - 2.64 x 10~3 M - 1.50 x 10~3 M*
+2.77 x 10~8 M3Q , R2 = 0.25 (9)
An I?2 = -2.11 + 2.92 x 1Q~2 M^ - 7.24 x 10~5 M2g
- 2.16 x 10~8 M3g + 2.68 x 1Q~2 M?0 - 1.80 x 10~4 M2Q
"7 Q O / O
+ 2.50 x 10 M^Q + 3.30 x 10 M?1 + 1.06 x 10 M^
- 6.27 x 10~8 M3^ , R2 = 0.30 (10)
An I?3 = -2.55 - 4.24 x 10~2 M6g + 2.26 x 10~4 M^g
- 3.56 x 10~7 M3g + 3.07 x 10~3 M?() - 3.65 x 1Q~5 M2Q
+ 6.14 x 10~8 M3Q + 2.47 x 10~2 M?1 - 8.14 x lo"5 M^j^
+ 7.85 x 10"8 M^ + 5.07 x lo"3 M?2 - 4.55 x 10~6 N^
+ 1.86 x 10~9 M32 , R2 = 0.42 (11)
where An I = Natural logarithm of basic intake rate for year of
subscript, cm/hr
M = Dry manure application for year of subscript, MT/ha.
R = Coefficient of multiple correlation
Data from all plots were used to generate the intake rate equation for
1970. Data for the residual plots, those receiving manure the first
year only, were omitted from the 1971, 1972, and 1973 analyses. Al-
though the equations explain only 16 to 42 percent of the variation
between basic intake rate and manure application rate, the correlation
coefficients were statistically significant at the 0.01 level.
118
-------
Yearly basic intake rates were calculated from Equations 8-11 assuming
constant yearly manure applications. For 1970, basic intake rate
gradually decreased as manure application increased. Basic intake rate
increased with increasing annual manure application up to 262 and 93
metric tons per hectare for 1971 and 1972, respectively, and then de-
creased. For 1973, basic intake rate decreased slightly as annual
manure application increased from 0 to 55 metric tons per hectare,
increased for annual manure applications of 55 to 269 metric tons per
hectare, and decreased for higher manure applications.
The increase in basic intake rate for the lower to medium annual manure
applications was attributed to an increase of organic matter in the
soil. Decreases in basic intake rate for high annual manure applications
were due to increased levels of sodium and potassium in the soil.
Although the basic intake rate prediction curve for 1973 was anticipated
to be similar to 1971 and 1972 with a peak at a lower annual manure
application rate, rainfall during November through March preceding the
1973 growing season (41.35 cm) leached salts downward in the soil pro-
file, reducing the detrimental effects on basic intake rate.
The basic rates for the residual manure treatments were depressed in
1970. However, basic intake rates were equal to or higher than the
control plots in subsequent years.
119
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SECTION XIV
ECONOMICS OF WASTE APPLICATION TO LAND
GENERAL
Feedlot wastes may be applied to land with waste disposal as the main
objective or they may be applied as a fertilizer to increase crop
yields. The most economical rate for applying feedlot runoff and
manure to land at the Pratt Feedlot, Inc. was determined.
METHODS AND PROCEDURES
Corn forage yield prediction equations were developed for annual appli-
cations of feedlot runoff and for annual and single year applications of
feedlot manure from data collected in the studies described in Sections
VIII and IX of this report.
Equations were developed to determine annual net income from crop pro-
duction on the area required for disposal of wastes at the Pratt
Feedlot, Inc. It was assumed that land area for waste disposal was
unlimited and that no other fertilizer was used. The most economical
waste application rates were determined from the net income equations
using yield prediction equations and 1974 prices.
Maximum net income results when the return from the last unit of fer-
tilizer added is equal to its cost. As a larger volume of material
must be applied to supply a unit of plant nutrient through feedlot
waste than through commercial fertilizer, it was assumed that wastes
would be spread onto land near the feedlot to keep hauling costs to a
minimum and that wastes would be the only fertilizer used. Equations
were developed to determine net income per hectare from corn pro-
duction using feedlot wastes as fertilizer. The most profitable waste
application rates were determined by substituting yield prediction
equations and 1974 prices into the net income equations.
120
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RESULTS AND DISCUSSION
Feedlot Runoff Disposal
The following corn forage yield prediction equations were
the runoff disposal studies:
Y?0 = 0.498 E + 41.5 , R2 = 0.32
Y?1 = -0.0164 E2 + 0.85 E + 36.3 , R2 = 0.37
Y?2 = -0.02898 E2 + 1.278 E + 49.2 , R2 = 0.27
Y?3 = -0.01696 E2 4- 0.98 E + 33.8 , R2 = 0.33
developed from
(12)
(13)
(14)
(15)
where Y?0 = Corn forage yield in year of subscript, MT/ha.
E = Annual runoff application, cm
R = Coefficient of multiple regression
In 1970, yields continued to increase as feedlot runoff application rates
increased up to the heaviest treatment which was 35 cm. The positive
effect on yield was attributed to increased availability of plant nu-
trients throughout the growing season. Maximum predicted yields re-
sulted from annual feedlot runoff applications of 26 cm in 1971, 22 cm
in 1972, and 29 cm in 1973. As yield depression at the higher feedlot
runoff application, rates was due to salt buildup in the soil, the lower
yield depression in 1973 was due to leaching of salts downward by the
above normal rainfall.
Annual net income from farming operations to dispose of effluent from
runoff catchment reservoirs where no additional fertilizer is added can
be expressed as:
I = P.YA - C A - C EA (16)
n f P e
where I = Annual net income, $
n
P = Selling price of corn forage, $/MT
Y = Corn forage yield, MT/ha.
A = Area farmed, ha.
C = Cost of corn forage production, $/ha.
p
C = Cost of applying runoff, $/ha.-cm
e
E = Annual runoff application rate, cm
The cost of corn production can be expressed as:
C = Cf + C, + C.
p t i i
121
-------
where Cf = Cost of field operations, $/ha.
C- = Cost of land, $/ha.
C = Cost of irrigation, $/ha.
The cost of irrigation is:
C± - CwW (18)
where C = Cost of applying water, $/cm
w
W = Depth of water applied, cm
Assuming the runoff applied reduces the amount of irrigation water
needed, the cost of irrigation becomes:
C. = C (W-E) (19)
i w
The area farmed to dispose of the runoff is:
A Te (20)
A=~E
where T = Annual runoff from feedlot, ha.-cm
e
Upon substituting Equations 17, 18, 19, and 20 into Equation 16, the
annual net income becomes:
P YT T
The selling price of corn forage was $15 per MT. Equations 12
to 15 predict corn forage yield. The cost of field operations which
includes tillage, planting, and weed control was $125 per ha.
The cost of land which includes interest on the investment and property
taxes was $200 per hectare. Although the cost of irrigation, in-
cluding depreciation on the system, interest on the investment, and
operating costs, is quite variable, it was assumed to be $4 per hectare-
centimeter (ha.-cm) for the Pratt area which has an average annual
irrigation requirement of 40 cm. As feedlot runoff can be applied
through the irrigation system, the cost of applying runoff was assumed
to be the same as for irrigation water. Total runoff available for
annual disposal was considered to be constant for a given feedlot.
The annual runoff application rate which gave maximum net income was
calculated for each year from Equation 21, using the above values for
the parameters. For each of the four years, maximum net income resulted
from the application of the first unit of runoff. These results are
122
-------
consistent with the results from most fertility studies which show that
crop yields increase at a decreasing rate as fertilizer application rates
increase.
Estimated cost of corn production was $485 per ha. Cost of corn pro-
duction would have had to exceed $622, $544, $738, and $507 per ha. for
1970 to 1973, respectively, before it would have been economical to
apply feedlot runoff with disposal as the main objective rather than
using it as a fertilizer.
When feedlot runoff is used as a fertilizer, net income per hectare can
be expressed as:
i = P..Y - C, - C- - C W + C E - C E (22)
H t I J. W w
where i = Net income, $/ha.
n
Maximum net income resulted from the feedlot runoff application rate
which gave highest yields. If the cost of applying feedlot runoff is
less than for applying irrigation water, maximum net income would result
from higher feedlot runoff application rates. On the other hand, if the
cost of applying feedlot runoff exceeds the cost of applying well water
or if supplemental irrigation is not practiced, maximum net income would
result from lower feedlot runoff application rates.
Manure Disposal—Annual Applications
The following corn forage yield prediction equations were developed from
the study area receiving annual applications of manure:
Y = -0.000127 M2 + 0.0583 M + 45.4 , R2 = 0.25 (23)
n
Y = -0.0001784 M2 + 0.0536 M + 37.5 , R - 0.49 (24)
. R2 = 0.48 (25)
Y = -0.0459 M + 60.2
Y = -0.0001488 M2 + 0.0556 M + 42.4
73
,2 j. n n«« M + 42.4 . R2 = 0.51 (26)
M = Annual manure application (dry weight), MT/ha.
where
(27)
= F^IA - a\<-jr T ^T ' "n" ~m~~~
"n
I = PfYA - A(Cf + C1 + C.) - CmMA
12.3
-------
where C = Cost of applying manure, $/MT
m
The area farmed to dispose of the manure is:
A = ^ (28)
where T = Annual manure from feedlot (dry weight), MT
m
Upon substituting Equation 28 into Equation 27, the annual net income
becomes:
P YT T
*n - -V - -i(Cf + °1 + V - CmTm <29>
Equations 23 to 26 predict corn forage yields. Cost of applying irriga-
tion water was $160 per hectare. Cost of applying manure to land
which includes cleaning of pens, hauling to the stockpile, loading from
the stockpile, hauling to fields, and spreading onto land was $4.95 per
metric ton. Manure application costs were based upon measurements
which show the average moisture content of manure taken from the stock-
pile was 33% on a dry weight basis and current manure handling costs
of $3.30 per MT of material. Other prices and costs were the same as
for the feedlot runoff analyses.
The annual manure application rate which gave maximum net income was
calculated for each year by Equation 29. As for feedlot runoff, maximum
net income resulted from the application of the first unit of manure.
Cost of corn production would have had to exceed $681, $562, $903 and
$636 per ha. for 1970 to 1973, respectively, before it would have been
economical to apply manure with disposal as the main objective rather
than using it as a fertilizer.
When manure is used as a fertilizer, net income per hectare becomes:
i - P.Y - C. - C, - C. - C M (30)
n f f 1 i m
For each of the four years, cost of applying manure exceeded income from
the manure. Cost of applying manure would have had to have been $0.87,
$0.80, $0.69 and $0.83 per MT for 1970 through 1973, respectively,
before it would have been profitable to apply the first unit of manure.
There are two possible reasons why returns from annual manure applica-
tions were less than costs of applying manure. First, the soil had a
high initial fertility level as evidenced by high yields from the check
plots throughout the study. Secondly, available nitrogen may have been
limiting under low annual manure applications. Herron and Erhart
found that 50% of the nitrogen in feedlot manure was removed by sorghum
124
-------
the first year after it was applied. Manure at low annual application
rates may not have provided sufficient available nitrogen for optimum
corn growth during the study.
Manure Disposal—First Year Only
The following corn forage yield prediction equations were developed from
the study area receiving manure the first year only:
Y?0 = -0.000127 M2 + 0.0583 M + 45.4 , R2 = 0.25 (31)
Y = -0.0000991 M2 + 0.0638 M + 34.1 „ R2 = 0.21 (32)
Y?2 = -0.0000561 M2 + 0.0364 M + 54.8 , R2 = 0.16 (33)
Y?3 = -0.000106 M2 + 0.0947 M + 32.0 , R2 = 0.69 (34)
Maximum predicted yields resulted from first year only applications of
230, 322, 324 and 447 MT/ha. for 1970 through 1973, respectively.
As manure was added the first year and no other fertilizer was added in
subsequent years, increases in corn forage yield from manure during the
study were due to the first year's application. Net income from manure
was determined from Equation 30 using the same prices and costs as for
annual manure applications. The corn forage prediction equations sub-
stituted into Equation 30 were Equation 31, Equations 31 plus 32,
Equations 31 plus 32 plus 33, and Equations 31 plus 32 plus 33 plus 34
for 1970 through 1973, respectively.
At the end of the 1973 season, accumulated returns from manure were
insufficient to pay application costs of $4.95 per MT. However,
returns were sufficient to pay for the first unit of manure at an appli-
cation cost of $3.80 per MT. The 1974 yield prediction equation indi-
cates residual effects from the single year's application of manure
will continue to increase corn forage yields in the future. It appears
that increased yields from the manure in subsequent years will make for
profitable manure use as a fertilizer.
125
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SECTION XV
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132
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SECTION XVI
PUBLICATIONS
1. Manges, H. L., L. A. Schmid, and L. S. Murphy. Land Disposal of
Cattle Feedlot Wastes. In: Livestock Waste and Pollution
Abatement, Proceedings of the International Symposium on
Livestock Wastes. Amer. Soc. of Agri. Engrs., St. Joseph,
Michigan, 1971.
2. Ohmes, F. E. Equations for Runoff From Furrow Irrigation. Un-
published M.S. Thesis. Kansas State University Library,
Manhattan, Kansas, 1971.
3. Fields, W. J. Hydrologic and Water Quality Characteristics of
Beef Feedlot Runoff. Unpublished M.S. Thesis. Kansas State
University Library, Manhattan, Kansas, 1971.
4. Murphy, L. S., G. W. Wallingford, W. L. Powers, and H. L. Manges.
Effects of Solid Beef Feedlot Wastes on Soil Conditions and
Plant Growth. In: Waste Management Research, Proceedings
1972 Cornell Agricultural Waste Managemtn Conference.
Graphics Management Corp., Washington, D. C., 1972.
5. Ohmes, F. E. Estimating Runoff from Furrow Irrigation. ASAE
Paper No. 72-229, St. Joseph, Michigan, 1972.
6. Manges, H. L., L. S. Murphy, and E. H. Goering. Disposal of Beef
Feedlot Wastes onto Cropland. ASAE Paper No. 72-961, St.
Joseph, Michigan, 1972.
7. Powers, W. L., R. L. Herpich, L. S. Murphy, D. A. Whitney, and
H. L. Manges. Guidelines for Land Disposal of Feedlot Lagoon
Water. C-485, Cooperative Extension Service. Kansas State
University, Manhattan, Kansas, 1973.
8. Manges, H. L., L. S. Murphy, and W. L. Powers. Summary of Kansas;
Experience with Liquid Waste Spreading. In: Proceedings of
Midwest Livestock Waste Management Conference. Iowa State
University, Ames, Iowa, 1973.
133
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9. Murphy, L. S., G. W. Wallingford, and W. L. Powers. Effects of
Application Rate in Direct Land Disposal of Animal Wastes.
J. Amer. Dairy Sci. Assoc. 56(10):1367-1374, 1973.
10. Stritzke, R. D. Effects of Heavy Feedlot Manure Application Rates
on the Basic Infiltration Rate of Soil. Unpublished M.S.
Thesis. Kansas State University Library, Manhattan, Kansas,
1973.
11. Wallingford, G. W., L. S. Murphy, W. L. Powers, and H. L. Manges.
Effect of Beef-Feedlot-Lagoon Water on Soil Chemical Properties
and Growth and Composition of Corn Forage. J. Environ. Qual.
3(l):74-78, 1974.
12. Wallingford, G. W., L. S. Murphy, W. L. Powers, H. L. Manges, and
L. A. Schmid. Use of Cattle Feedlot Runoff in Crop Production.
In: Wastewater Use in the Production of Food and Fiber—Pro-
ceedings. Environmental Protection Technology Series EPA-
660/2-74-041. U.S. Government Printing Office, Washington,
D. C., 1974.
13. Harris, M. E. Characteristics of Runoff from Disposal of Cattle
Feedlot Wastes on Land. Unpublished M.S. Thesis. Kansas
State University Library, Manhattan, Kansas, 1974.
14. Powers, W. L., G. W. Wallingford, L. S. Murphy, H. L. Manges, and
H. E. Jones. Guidelines for Applying Beef Feedlot Manure to
Fields. C-502, Cooperative Extension Service. Kansas State
University, Manhattan, Kansas, 1974.
15. Wallingford, G. W. Effects of Solid and Liquid Beef Feedlot Wastes
On Soil Characteristics and on Growth and Composition of Corn
Forage. Unpublished Ph.D. Thesis. Kansas State University
Library, Manhattan, Kansas, 1974.
16 Manges, H. L., D. E. Eisenhauer, R. D. Stritzke, and E. H. Goering.
Beef Feedlot Manure and Soil Water Movement. ASAE Paper
No. 74-2019, St. Joseph, Michigan, 1974.
134
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SECTION XVII
GLOSSARY OF ABBREVIATIONS AND SYMBOLS
ABBREVIATIONS
BOD
BOD5
cm
cm/hr
cm/yr
COD
DTPA
EC
g
ha.
ha. -cm.
JTU
kg
kg/ha.
km
m
meq
ml/min
mmhos/cm
MT/ha.
MT/ha./yr
No.
ppm
r
R2
SS
TS
VS
SYMBOLS
C
Ca
biochemical oxygen demand
5 day biochemical oxygen demand
centimeter
centimeter per hour
centimeter per year
chemical oxygen demand
Diethylene Triamine Penta Acetic Acid
electrical conductivity
gram
hectare
hectare-centimeter
Jackson Turbidity Units
kilogram
kilogram per hectare
kilometer
meter
milliequivalent
• milligrams per liter
• milliliter per minute
• millimhos per centimeter
• metric ton per hectare
- metric ton per hectare per year
• number
- parts per million
• correlation coefficient
- coefficient of multiple regression squared
- suspended solids
- total solids
- volatile solids
carbon
calcium
methane gas
135
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Ci — chloride
C02 — carbon dioxide gas
C02 - C — carbon dioxide - carbon
Cu -- copper
pe — iron
H20 — water
K — potassium
g+ — potassium monovalent cation
Mg — magnesium
Mn — manganese
N — nitrogen
N2 — nitrogen gas
N20 — nitrous oxide gas
Na — sodium
jja+ — sodium monovalent cation
NH -N — ammonia-nitrogen
— ammonium monovalent cation
— ammonium-nitrogen
NOg-N ~ nitrite-nitrogen
NO^-N — nitrate-nitrogen
0, — oxygen gas
£ __ tne negative logarithm of the concentration of
the hydrogen ion in gram atoms per liter
p — phosphorus
S — sulfur
Zn " zinc
OQ — degree centigrade
# — number
% — percent
136
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing]
REPORT NO.
EPA-660/2-75-013
3. RECIPIENT'S ACCESSI Of* NO.
TITLE AND SUBTITLE
TREATMENT AND ULTIMATE DISPOSAL OF CATTLE FEEDLOT WASTES
5. REPORT DATE
April, 1975 (approval)
6. PERFORMING ORGANIZATION CODE
. AUTHOR(S)
Harry L. Manges, Ralph I. Lipper, Larry S. Murphy,
William L. Powers, Lawrence A. Schmid
8. PERFORMING ORGANIZATION REPORT
PERFORMING ORGANIZATION NAME AND ADDRESS
Kansas State University
Manhattan, Kansas 66505
10. PROGRAM ELEMENT NO.
1BB039
11. CONTRACT/GRANT NO.
S800923
2. SPONSORING AGENCY NAME AND ADDRESS
U. S. Environmental Protection Agency
Robert S. Kerr Environmental Resaerch Laboratory
P. 0. Box 1198
Ada, Oklahoma 74820 __
13. TYPE OF REPORT AND PERIOD COVERED
Final Report
14. SPONSORING AGENCY CODE
5. SUPPLEMENTARY NOTES
6. ABSTRACT
A study was conducted to determine the characteristics of beef feedlot wastes both
runoff and manure, and the optimum application rate of these wastes to land. The
project was located at a commercial beef feedlot in southcentral Kansas.
Characteristics of beef feedlot wastes varied widely with season.
Near maximum corn forage yields, without excessive accumulation of salt £ £« °o11'
were obtained from waste application rates necessary to meet nitrogen fertilizer
"commendations. At these waste application rates, basic intake «" of water xnto
the soil was increased. Net income from irrigated corn production was sufficient
to make application of feedlot manure with disposal as the main objective unprofitable
Land application rates of beef feedlot wastes should be based uP°n. %r"u^1^d at
laboratory analyses of wastes from each feedlot. Feedlot wastes shoulbe applied at
rates necessary to meet nitrogen fertilizer recommendations. A salt-al^lx test
should be made annually on the surface soil to monitor changes in soil salinity
levels.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.lDENTIFIERS/OPEN ENDED TERMS
COS AT I Field/Group
Anaerobic-Lagoon, Land-Disposal, Waste-
Disposal, Water-Pollution, Cattle, Animal
Wastes, Manures, Rainfall, Soil Chemistry,
Soils, Fertilization, Groundwater, Ultimati
Disposal, Treatment Disposal
Water Pollutants,
Great Plains, Environ-
ment
02/01
02/03
13. DISTRIBUTION STATEMEN1
Unlimited Release
19. SECURITY CLASS (This Report)
148
20. SECURITY CLASS (Thispage)
22. PRICE
EPA Form 2220-1 (9-73)
U.S. GOVERNMENT PRINTING OFFICE; I975-698-636 ;t60 REGION lo
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