EPA-660/2-75-015
JUNE 1975
                      Environmental Protection Technology Series
Pollution  Abatement from  Cattle
Feedlots in  Northeastern  Colorado
and Nebraska
                                   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.   Socioeconomic 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, EPA, and approved for publication.  Approval  does
not signify that the contents necessarily reflect the views and
policies of the Environmental Protection Agency, nor does  mention
of trade names or commercial products constitute endorsement or
recommendation for use.

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                                                                      y
                                        EPA-660/2-75-015
                                        JUNE  1975
    POLLUTION ABATEMENT FROM CATTLE FEEDLOTS
       IN NORTHEASTERN COLORADO AND NEBRASKA
                        By
                   L.  K. Porter
                 F.  G.  Viets, Jr.
                   T.  M. McCalla
                   L.  F. Elliott
                  F. A. Norstadt
                    H.  R. Duke
                   N.  P. Swanson
                   L.  N. Mielke
                 G.  L.  Hutchinson
                   A.  R. Mosier
                   G.  E. Schuman
         U.  S.  Department of Agriculture
          Agricultural Research Service
          Fort  Collins, Colorado  80521
               Grant EPA-IAG-D4-0446
             Program Element 1BB039
                    21 BEQ/012
                 Project Officers

               Mr.  Lynn R.  Shuyler
      U. S. Environmental Protection Agency
Robert S. Kerr Environmental Research Laboratory
              Ada,  Oklahoma  74820

                  Dr.  C.  E.  Evans
          Agricultural Research Service
         U. S. Department of Agriculture
          Fort Collins,  Colorado  80521
     NATIONAL ENVIRONMENTAL RESEARCH CENTER
       OFFICE OF RESEARCH AND DEVELOPMENT
      U. S. ENVIRONMENTAL PROTECTION AGENCY
            CORVALLIS,  OREGON  97330

           For Sale by the National Technical Information Service,
           U.S. Department of Commerce, Springfield, VA 22151

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                             ABSTRACT
     Climatic factors, feedlot runoff, and organic material in the
runoff were evaluated in experimental and commercial feedlots.  The
effects of slope, stocking rates, terraces, basins, and holding
ponds were evaluated to obtain the best controls for containing runoff.
In eastern Nebraska, 70 cm annual precipitation produces 23 cm of
runoff; whereas, in northeastern Colorado, 37 cm annual precipitation
gives only 5.5 cm of runoff.  Large applications of runoff liquid, up
to 91 cm on grass-Ladino and 76 cm on corn, in Nebraska did not de-
crease yields; however, in northeastern Colorado, the concentrated
high-salt runoff required dilution before direct application to crops.
The organic manure-soil interface severely restricts the movement of
water, nitrates, organic substances, and air into the soil beneath
feedlots.  The amounts of NOs-N in soil cores taken from Nebraska
feedlots and croplands ranked as follows:  abandoned feedlots > feed-
lot cropland > upland feedlots > river valley feedlots > manure
mounds > alfalfa > grassland.  Feedlots contribute Nti^t amines, car-
bonyl sulfide, ^S, and other unidentified substances to the atmos-
phere.  Ammonia and amine can be scavenged from the air by green
plants and water bodies.   Anaerobic conditions in feedlots are con-
ducive to the production of carbonyl sulfide, H2S, and amines.
Management practices, such as good drainage,  that enhance aeration
will decrease the evolution of these compounds.
                               ii

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                               CONTENTS

 Sections

 I      Introduction                                               1

 II     Summary                                                    2

 III    Conclusions                                                4

 IV     Recommendations                                            8

V      Descriptions of Field Sites, Special facilities,           13
       and Methods

VI     Composition and Amount of Runoff Including Relation        26
       To Climatic Variables, Slope, Stocking Density,
       Site, Site Codification

VII    Disposal of Runoff                                         39

VIII   Composition of Soil Solution and Soil Atmosphere           56
       Beneath Feedlots

IX     Investigations on Methods of Extraction of Nitrate         81
       From the Soil Profiles of Abandoned Feedlots

X      Airborne Pollutants                                        84

XI     References                                                 106

XII    List of Publications                                       111
                                 iii

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                                FIGURES

 No.                                                                Page

 1     Caisson  Before  Installation  in  the  Soil                       14

 2     Installed  Suction  Cup Assemblies and  Gas  Samplers             15

 3     Vacuum Lysimeter Ready  to  be Lowered  into Position            20
      Near  Center  of  Flat  (Anderson)  Feedlot

 4     Sloping  (Ashlind)  Feedlot  Immediately Following               22
      6.6 cm of  Rainfall,  June 1970.  Note  Diversion
      Dike  in  Left Center  of  Photo and Extremely Viscous
      Liquid Draining Toward  Flume in Immediate Foreground

 5     Access Tunnel,  Experimental  Feedlot,  Prior to Back-           24
      fill  and Completion  of  Feeding  Apron

 6     Design of  Experimental  Feedlot  and Arrangement of             25
      Soil  Fill  (1—clay loam, 2—sand, 3—clay loam over
      sand,  and  4—sand  over  clay  loam) in  Pits

 7     Rainfall,  Runoff,  and NH^-N  and N03-N Concentrations          28
      in Runoff, Sloping Cattle  Feedlot, Gretna, Nebraska,
      April  18,  1970

 8     Rainfall,  Runoff,  and NH^-N  and N03-N Concentrations          29
      in Runoff, Sloping Cattle  Feedlot, Gretna, Nebraska,
      April 19,  1970

 9     Rainfall,  Runoff,  and NH^-N  and N03-N Concentrations          30
      in Runoff, Sloping Cattle  Feedlot, Gretna, Nebraska,
      September  23, 1970

 10   Precipitation-Runoff Relationship for Sloping                 36
      (Ashlind)  Feedlot

 11   Average N03-N Levels in the  Soil Solution Extracted           60
      from the Broad-basin Terraced Feedlot at Increments
     of Depth and Time,  Springfield,  Nebraska, 1970-1971

12   Average N03-N Levels in the Soil Solution Extracted           61
     from the Broad-basin Terraced Feedlot at Increments
     of Depth and Time,  Springfield,  Nebraska, 1970-1971
                                 iv

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13   Average Soil-Gas Composition from 1 to 10 ft Beneath          62
     the Basin, Broad-basin Terraced Feedlot, Springfield,
     Nebraska, 1970-1971

14   Water Content Profile Near Center of Lot at Sloping           71
     Site

15   Average Nitrate Distribution Values in the Profiles           78
     of Sloping-upland, Flat Manure Mounds, and Abandoned
     Feedlots

16   Experimental Plot Layout on Abandoned Feedlot                 82

17   Distillable N Absorption from the Air Around a Small          86
     Feedlot and Adjacent Cropland at Central City, Nebraska

18   Nondistillable N Absorbed by the Trapping Solution            88
     at Central City, Nebraska

19   Distillable N Volatilized from Pastured Cattle and            89
     Cropland Near Treynor, Iowa

20   Foliar C02 and NH3 Uptake Rates of Soybean (final             91
     leaf surface area, 89 cm2)

21   NH3 Uptake Rates Predicted by Equation Ca/ra + rs             93
     vs. NHs Uptake Rates Measured Experimentally.  The
     Diagonal Line Through The Graph Represents All
     Points with Equal Coordinates.
22   Effect of Amine Concentration on C. e£&qo60/utea               97
     Population Growth
23   Effect of Methyl Amine on C. etttpiotdea Amraonium-N           98
     Uptake

24   Effect of Methyl Amine on C. e£U,pt>o£de,& Photo                100
     synthetic 02 Production

25   Effect of Methyl Amine on C. eJttipAOJ.de.0. Respira-             101
     tory 02 Consumption

26   Production of Carbonyl Sulfide (COS) and Dihydrogen           104
     Sulfide (H2S) from Anaerobically Incubated Manure
     and Compost

27   Gases Present Above Anaerobically Incubated Manure            105
     and Compost

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                                TABLES

 No_»_                                                               page

 1    Summary of Runoff Events  from Teedlot  Pen,  Gretna,             27
      Nebraska,  1968-1972

 2    Solids  Accumulations Removed  from Basins  of Teedlot            32
      Terraces with  Contributing Areas of "Varying Slope and
      Slope Lengths,  Omaha and  Springfield,  Nebraska,  July 1971

 3    Ranges  in  the  Characteristics and Chemical  Values of           34
      Runoff  from Beef  Cattle Teedlots, Mead, Nebraska,
      1968-1972

 4    Quantity of Materials Removed in Runoff from Beef              35
      Cattle  Feedlot, Mead, Nebraska,  1969-1972

 5    Chemical Elements  in Runoff from Beef  Cattle Feedlots,         37
      Mead, Nebraska

 6    Annual  Precipitation and Runoff  - Ashlind                      37

 7    Chemical Composition of Runoff from Feedlots near              38
      Fort Collins, Colorado

 8    Feedlot Effluent and Water Applications to  Grass and           42
      Clover  Plots, Silty Clay Loam Soil, Springfield,
      Nebraska,  1970-1972

 9     Quantities  of Solids and Nutrients Applied  to Grass-           44
      clover, Cockerill Feedlots, Springfield, Nebraska,
      1970-1972

10   Forage Yields and Total Nitrogen Contents, Grass and           45
     Contents, Grass and Clover Effluent Disposal Plots,
     Springfield, Nebraska, 1971-1972 a

11   Total Quantities of Solids, Nutrients and Salts Applied        47
     to Corn Plots Receiving Maximum Rates of Effluent
     Application Springfield, Nebraska, 1970-72a (kg/ha)

12   Corn Grain and Stover Yields from Effluent Disposal  Plots,      48
     Cockerill Feedlots, Springfield, Nebraska, 1972

13   Characteristics of the Effluent and Total Quantities of       50
     Nutrients and Solids Applied to -Forage Sorghum Plots in 1971
     and 1972, Springfield,  Nebraska
                                  vi

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 14   Forage  Sorghum Yields  for  1971 and 1972  (metric               51
     tons  dry matter/hectare)

 15   Nitrate-N Contained in Torage Sorghum Harvested in            52
     1971  and 1972  (ppm)

 16   Average Yearly Concentrations of Some Nitrogen Compounds      56
     in the  Soil  Solution Beneath a Teedlot and a Cropped
     Field (yg/ml)

 17   Average Soil Atmosphere Composition at Tarious Soil           58
     Depths  Beneath a Teedlot and Cropped Tield for a
     1-Year  Period  (% by volume)

 18   Nitrate and  Nitrite Nitrogen and Eclectrical Conductivity     63
     of Soil Solutionsa Obtained from Caissons at Ashlind
     Feeders, Inc., Tort Collins, Colorado

 19   Chemical Oxygen Demand, Phosphate, and pH of Soil Solutions3  64
     Obtained from  Caissons at Ashlind Feeders, Inc., Fort
     Collins, Colorado

 20   Nitrate and  Nitrite Nitrogen, Electrical Conductivity,        65
     Chemical Oxygen Demand, Phosphate, and pH of Water
     Samples Obtained from  Several Sources in the Area of
     the Caissons at Ashlind Feeders, Inc., Fort Collins,
     Colorado

 21   Characteristics of Soil Taken from Near the Center            66
     Caisson at Ashlind Feeders, Inc., Fort Collins, Colorado

22   Soil Water Tensions (Centibars) as Quarterly Averages         67
     Found in the Alfalfa Caisson at Ashlind Feeders, Inc.,
     Fort Collins, Colorado

23   Soil Water Tensions (Centibars) as Quarterly Averages         67
     Found in the Bunk Caisson at Ashlind Feeders, Inc.,
     Fort Collins, Colorado

24   Soil Water Tensions (Centibars) as Quarterly Averages         68
     Found in the Center Caisson at Ashlind Feeders, Inc.,
     Fort Collins, Colorado

25   Average Soil Atmosphere Composition (Percent by Volume)       68
     Beneath a Cropped Field and Feedlot for Two Years3
     at Ashlind Feeders, Inc.,  Tort Collins, Colorado
                                 vii

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26   Chemical Composition of Leachates Obtained from               72
     Vacuum Lysimeters in Feedlots Near Port Collins,
     Colorado

27   Changes of Composition of Lysimeter Leachates with            72
     Time from Center of Anderson Teedlot

28   Nitrate and Nitrite Nitrogen, Electrical Conductivity         74
     and pH of Soil Solutions Obtained from Lysimeters of
     Experimental Feedlot at Tort Collins, Colorado, Rigden
     Farm, Colorado State University

29   Average Soil Atmosphere Composition (Percent by               75
     Volume) of Experimental Feedlot Site

30   Average Quantity of Nutrients in a 9.1 m Profile              79
     Under the Different Feedlot and Crop Management Systems
     Investigated  kg/ha.

31   Yields and Nitrogen Uptake of the Alfalfa and Corn on         83
     an Abandoned Feedlot

32   Aliphatic Amines Identified as Feedlot Volatiles and          95
     Their Concentrations Relative to Ammonia

33   Statistics Relating Algal Population to Amine Concentration   96

34   Total Distillable N and Aliphatic Amine Content of a          102
     Lake Located Near a Cattle Feedlot3
                                 viii

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                            ACKNOWLEDGMENTS
Agricultural Research Service scientists express their sincere
appreciation to:

The management of Underwood Farms, Omaha, Nebraska, and to T. C. Reeves,
Central City, Nebraska, for their continued cooperation, assistance, and
access to their feedlots and premises.

William and Joyce Cockerill, Springfield, Nebraska, and Howard and
Harland Krambeck, Gretna, Nebraska, for their assistance and cooperation
with the research associated with feedlot runoff control and disposal
conducted on their farms.

Rodney Weeth, Gretna, Nebraska, for contributing a portion of an
established feedlot for the conduct of a study on abandoned feedlots.

William Krula, Rogers, Nebraska, for cooperation with a control system
requiring the use of a sump and pump to discharge runoff effluent to a
holding pond and to the Maple Creek District and Soil Conservation
Service for their contributions.

Ashlind Feeders, Inc., Fort Collins, Colorado, for their cooperation in
allowing access to their feedlots and surrounding cropland.

John A. Anderson and Son, Fort Collins, Colorado, for cooperation in
allowing access to their feedlot.

The following operators in Nebraska who permitted access to their
feedlots for purposes of obtaining soil cores:

Cuming County:      Herb Albers and Son
                    Gail Anderson
                    Dave Griffin
                    Louis Luebbert
                    Marvin Prinz
                    Bob Schmaderer

Douglas County:     Underwood Farms, Inc.
                    A. E. Ruser and Sons
                    Paul E. Pooley

Sarpy County:       William R.  Cockerill
                    James (Phil) Latham
                    Louis Timmerman and Sons
                    John Ward
                    Rodney Weeth
                                 ix

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Polk County:        Augustin Brothers

Personnel of the departments of Agronomy, Agricultural Engineering,
and Animal Science at University of Nebraska and Colorado State Univer-
sity, respectively, and their Agricultural Experiment Stations for their
continued assistance and consultation.

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                                 PREFACE

     This report summarizes research findings and fulfills all the re-
quirements of the Interagency Agreement EPA-IAG-D4-0446 between the U. S.
Department of Agriculture, Agricultural Research Service and the Environ-
mental Protection Agency, covering the 4^-year period ending June 30,
1974, and involving a jointly-financed research program and plan of
operation as set forth in the proposal "Pollution abatement from cattle
feedlots in Northeastern Colorado and Eastern Nebraska" submitted by Dr.
C. E. Evans, ARS, Fort Collins, Colorado, on May 9, 1969, and as amended
June 27, 1972.  The overall research objectives were:

     1.  To determine the extent and kinds of microbial, chemical and
         organic pollutants entering the atmosphere, soils, and sur-
         face and underground water supplies from cattle feedlots in
         two contrasting climatic zones (Northeastern Colorado with
         annual precipitation of 14-15 inches and Eastern Nebraska
         with annual precipitation of 27-28 inches); and

     2.  To evaluate different feedlot management systems as to their
         effectiveness and efficiency in disposing of both liquid and
         solid wastes under two different climatic conditions.

     This research program was conducted under a memorandum of agreement
(Grant 13040 DPS) between the Federal Water Pollution Control Adminis-
tration (a predecessor of EPA) and ARS during Fiscal Years 1970 and 1971,
and under interagency agreements EPA-IAG-0200(D) in FY 1972, EPA-IAG-
135(D) in FY 1973, and EPA-IAG-D4-0446 in FY 1974.

     Ronald R. Ritter, Kansas City, Missouri, served as Project Officer
for EPA during Fiscal Years 1970, 1971, and 1972; Lynn R. Shuyler, Ada,
Oklahoma, served as Project Officer for EPA during Fiscal Years 1973 and
1974; and C. E.  Evans, Fort Collins, Colorado, served as ARS Project
Officer.

     Scientists of the Agricultural Research Service who were involved
in the conduct of various phases of this research were:

     Fort Collins, Colorado                 Lincoln, Nebraska
     Francis E.  Clark                       Lloyd F. Elliott
     Harold R. Duke                         James R. Ellis
     Howard R. Haise                        C. L. Linderman
     Gordon L. Hutchinson                   Jeffery C.  Lorimer
     E. Gordon Kruse                        T. M. McCalla
     Arvin R.  Mosier                        Lloyd N. Mielke
     Fred A. Norstadt                       G. E. Schuman
     Sterling R.  Olsen                      Norris P.  Swanson
     Lynn K. Porter
     Frank G.  Viets
                                     xi

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                                SECTION I

                              INTRODUCTION
 This  report  is  a summary of cooperative  investigations made January,
 1970,  through June  30,  1974, between  the Agricultural Research Service
 and the Nebraska and  Colorado State Agricultural Experiment Stations with
 the financial support of the Environmental Protection Agency.  Many of
 the studies  have not  been completed,  and therefore, only progress re-
 ports  are  given.  Many  parts of  the investigations have been  completed,
 and the methodology and results  are reported  in the papers listed in the
 List  of Publications.

 The research was conducted at various field sites in central  and eastern
 Nebraska and in  northcentral Colorado and in  Agricultural Research Service
 Laboratories at  Lincoln,  Nebraska, and Fort Collins, Colorado.


 THE SPECIFIC OBJECTIVES  OF THE RESEARCH  WERE:

 (1)  To determine the extent and kinds of microbial, chemical, and
     organic pollutants  entering the atmosphere, soils, and surface
     and underground water supplies from cattle feedlots in two con-
     trasting climatic  zones (northeastern Colorado, with annual
     precipitation  of 35.6 to 38.1 cm (14 to  15 in.), and eastern
     Nebraska, with annual precipitation of 68.6 to 71.1 cm (27 to
     28 in.).

 (2)  To evaluate different feedlot management systems as to their
     effectiveness  and efficiency in disposing of both liquid and
     solid wastes under  two different climatic conditions.

Although the two areas have similar moderate  temperature regimes,
markedly differing precipitation permits comparison of precipitation
differences  on runoff, percolation, and profile aeration on otherwise
similar conditions.   In both areas, cattle are usually fed on earth-
surfaced lots at comparable rates of stocking.  The Nebraska research
sites are in the zone classed as dry by EPA, with a 25- to 75-cm
 (9.8 to 29.5 in.) annual deficit of potential evaporation over pre-
cipitation.  The Colorado  field sites are in the semiarid zone, with
a deficit exceeding 75 cm  (29.5 in.).

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                            SECTION II

                             SUMMARY


Two climatic zones  (northeastern Colorado, precipitation 35.6 to 38 cm,
and eastern Nebraska, precipitation 68 to 71 cm) were selected to study
the effect of climate, feedlot animal density, feedlot design, and feed-
lot management on the extent and movement of potential air and water
pollutants from feedlots.  The extent of water percolation and inorganic
and organic chemicals movement beneath feedlot soil surfaces was stud-
ied with specially  constructed caissons and vacuum lysimeters.  Climatic
factors were monitored with rain gages, anemometers, hydrothermographs,
evaporation pans, and maximum and minimum thermometers.  Detention
basins were constructed to retain runoff and equipped with water-level
recorders to record the duration, rate, and quantity of runoff.

In eastern Nebraska, 70 cm (27 inches)  of annual precipitation produces
23 cm (9 inches) of runoff, whereas in northeastern Colorado, 37 cm
(14.5 in.) annual precipitation produces only 5.5 cm (2.2 in.) of runoff.
The runoff in Colorado is highly concentrated, especially in salts,
and should not be applied directly to crops.  In Nebraska, large
applications of feedlot runoff have been applied directly to crops--
up to 91 cm (36 in.) on grass-Ladino and 76 cm (30 in.)  on corn--without
adverse effects.  In eastern Nebraska, feedlots should be designed to
control runoff and materials that can be transported by surface water.
This can be accomplished by controlling the degree and length of slope
in feedlots and utilizing diversion terraces and debris basins.  For
sloping feedlots, the degree and length of slope should not exceed by
more than three times that recommended for cropland.  Terraces and
mounds can be employed to restrict length of slope and improve drainage.
Basins can be used to collect runoff from feedlots.  Solid accumula-
tion in a basin should not exceed 20 cm (7.8 in) before removal.
Accumulations of feedlot solids greater than 20 cm results in long
drying times and odor problems.  The organic solids in runoff effluent
effectively seal the soil surface of basins, preventing water infil-
tration .

Data collected for water percolation and movement of nitrate and
organic pollutants beneath feedlots indicate that if the feedlot is
kept continuously stocked so as to maintain an intact manure layer,
there is little likelihood of nitrate  or other pollutants moving
through the soil profile to the water table.  An anaerobic layer
develops at the interface of the manure and the soil.   This interface
helps prevent the movement of nitrate  and water.  Caution should be
exercised in cleaning operations not to destroy this interface layer.
Abandoned feedlots contained more nitrate-N in their profile than
under any other conditions studied.  In a 9.1-meter (29 ft) profile,

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 there  was  7.2  metric tons  of N03-N per hectare  (3.2  tons/acre).  This
 was  almost 3.5 times the quantity of NOa-N  accumulated under  any other
 management system.   Feedlots which were  abandoned  and then  cropped
 showed some decrease in NOa-N levels.  Both corn and alfalfa  took up
 significant amounts  of nitrate from  abandoned feedlots.  Nitrate an-
 alyses of  corn plant materials showed high  levels  of
 Beef cattle  feedlots  can  contribute significant amounts of ammonia,
 amines,  and  odiferous sulfur  compounds to the atmosphere.  Such com-
 pounds  are potential pollutants to water surfaces and life (plant and
 animal)  in the vicinity of  the feedlot.  Ammonia and amines were
 trapped in acid.  Traps,  fabricated of wire mesh with a conical metal
 roof and a plywood  floor, were placed 1.5 m (4.9 ft) above the ground
 on posts.  Plastic  dishes (750 ml) filled with 0.01 N_ H2SOtt were placed
 inside  the trap.  This solution was changed every 1 to 3 weeks, depend-
 ing  on  evaporation, and analyzed  for distillable N  (ammonia and short-
 chained  amines) .  Amines  and  sulfur compounds were  analyzed by gas
 chromatography and  colorimetric techniques.  Significant amounts of the
 basic N-compounds volatilized were aliphatic amines,

 Aliphatic amines have the potential for altering metabolism and thus
 could affect water  ecosystems.  Chemical theory and observations sug-
 gested that  gaseous aliphatic amines can be absorbed by water exposed
 to low  atmospheric  concentrations of the compounds.  Microorganisms
 were found in lakes that degrade  aliphatic amines,  and during warm
 weather microbial activity was sufficient to inhibit amine accumulation.
 The effect of various concentrations of aliphatic amines on algal meta-
 bolism was studied.  Algae could not utilize amine-N for growth.  Algal
 photosynthesis is hindered while  respiration is enhanced by methyl
 amine.
Our research showed that significant amounts of NHa volatilized from
the surface of cattle feedlots and was absorbed by water, soil, and
plant surfaces in the vicinity of a feedlot.  Foliar NHa absorption
occurs readily and the data suggest it plays an important role in de-
contaminating the earth's atmosphere.  Calculations based on plant NH3
absorption rates showed that at normal atmospheric concentrations of
NH3, plant' canopies could absorb 20 kg N per hectare (17.8 Ib N per
acre) per year.

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                              SECTION III

                              CONCLUSIONS


COMPOSITION AND AMOUNT OF RUNOFF INCLUDING CLIMATIC VARIABLES, SLOPE,

STOCKING DENSITY, SITE, AND SITE MODIFICATION

About 5 cm (2 in.) of runoff is expected annually from feedlots in the
35-cm (.13.8 in.) precipitation area of northeastern Colorado.  At the
study site, the manure pack consistently absorbed the first 1 cm C-4 in.)
of precipitation, with an average of 45 percent of the precipitation
above 1 cm leaving the lot as surface runoff.  Because the studies at
Fort Collins were limited to a single site and relatively few runoff-
producing events were recorded during the study period, it is difficult
to establish, with confidence, the expected range of annual runoff. Over
the three years of record, runoff varied from less than 1 to 25 percent
of the annual precipitation, depending upon distribution and intensity of
precipitation.  Above 23 cm (9 in.) of runoff is expected from the 70-cm
(27.6 in.) annual precipitation in eastern Nebraska.  However, the pre-
cipitation over a period of years will vary from less than 50 cm (19.7
in.) to over 85 cm (33.5 in.) and annual runoff from a feedlot may vary
from less than 15 cm to 35 cm (5.9 to 13.8 in.).  Design of control
structures should be based upon the chronic wet periods of continuing
wet weather that may be expected over a 10-year period.

Pollution by runoff transport of materials from beef cattle feedlots
can be accomplished best by:  (1) control of the degree and length of
slope factor, utilizing diversions and terraces; (.2) use of debris basins
or solids traps to immediately separate readily settleable solids from
the effluent to eliminate problems of combined storage of the solids
and effluent; and (3) disposal of the solids and the effluent on
cropland.

DISPOSAL OF RUNOFF

In eastern Nebraska, feedlot runoff effluent is a highly variable, low-
grade fertilizer.  However, large and frequent applications can supply
much of the nutrient needs of many crops.  Annual applications up to
91 cm (35.8 in.) on grass-Ladino clover and 76 cm (29.9 in.) on corn
have not decreased and sometimes have increased yields.  Good growth of
the Ladino clover, a low-salt-tolerance crop, indicates salt accumula-
tion in the soil is not a problem.

Under northeastern Colorado conditions, the infrequent and very limited
runoff is of such concentrated composition that direct application to
growing crops would not be feasible.  Disposal on arable land would be
possible after sufficient dilution with irrigation water to reduce the
electrical conductivity to values acceptable for irrigation water.

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COMPOSITION OF SOIL SOLUTION AND SOIL ATMOSPHERE BENEATH FEEDLOTS

There was no marked movement of organic substances into the feedlot
as would be shown by increases in COD and PO^3".  This conclusion is
in agreement with a previously published report of Mosier et al. (1).
These authors concluded that there was no uniform or continuing
movement of organic compounds from the manure pack either into sub-
jacent soil profile or through that profile into the groundwater.
Nitrate and other soluble nitrogen-containing pollutants will perco-
late only a short distance downward from the lot surface in a continu-
ously stocked feedlot.  Significant percolation of water was detected
only at the flat site near Fort Collins, and then only immediately
following thorough scraping of the surface or significant drying of
the surface manure pack.  Most physical characteristics of the feedlot
interface severely restrict movement of air and water into the soil.
Microbial metabolism of organic matter near the feedlot surface
further depletes the oxygen supply.  This results in reduced con-
ditions in the feedlot soil profile which is favorable for denitrifi-
cation.  If a new feedlot is stocked continuously, initial nitrate
buildup will decrease, presumably due to denitrifi cation.  In areas
where denitrification occurs, there is usually a buildup of methane
in the soil profile beneath the feedlot.  Areas of the feedlot which
do not contain methane in the profile may contain appreciable
The management of feedlots is an important consideration to the accu-
mulation of N03-N in the soil profile and care must be exercised to
leave the interface layer intact when the feedlot is cleaned.  Feed-
lots should not be allowed to lie idle for long periods of time.

The N03-N content of soil profiles from abandoned feedlots, feedlot -
cropland, etc., were examined and ranked according to decreasing
average NOa~N in the soil cores:  abandoned feedlots > feedlot-cropland
> upland feedlot > river-valley feedlots > manure mounds > alfalfa
grassland.  Feedlots continuously stocked, under mounds, and flat
river-valley feedlots do not have problems with NOa-N accumulation
in the soil profile and would not likely contribute nitrate to the
groundwater.  A feedlot site that was abandoned for feeding and
left idle for 6 years contained more than 19 metric tons (20.9 tons)
of NOa-N per hectare to a soil depth of 9 meters (9.8 yd).   Another
feedlot site that was abandoned and cropped to alfalfa and corn for
about 14 years showed NOa-N content similar to cropland.

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INVESTIGATIONS ON METHODS OF EXTRACTION OF NITRATE FROM THE SOIL

PROFILES OF ABANDONED FEEDLOTS

The data collected to date indicate that growing alfalfa limited the
movement of nitrate below the root zone.  Corn also reduced the nitrate
movement; however, movement below the root zone of this crop occurred.
The alfalfa forage could be used for livestock feed, whereas the ni-
trate content of the corn forage was too high to be used as a feed
unless ensiled or mixed with other feed.  The alfalfa yields are much
greater than those of corn; therefore, the nitrogen removal from the
soil is greater.  No salt damage was evident on the plots planted
directly in the feedlot, and therefore, the removal of the top 15 cm
(5.9 in.) of feedlot soil may not be necessary).

AIRBORNE POLLUTANTS

Feedlots and even pastured cattle can contribute distillable N to the
atmosphere.  The majority of the distillable N was NH3; however, an
appreciable portion of the volatilized basic N-compounds was
aliphatic amines.

The importance of atmospheric NH3 as an agent for the transport and
redistribution of N both within and among ecosystems has been vastly
underestimated.  Cattle feedlots are apparently a major source of NH3
in the atmosphere.  Calculations based on the data collected indicate
that annual NH3 absorption by plant canopies growing in air containing
NHs at normal atmospheric concentrations could be about 20 kg/ha. (17.8
Ib/acre).  This rate of NH3 supply is large enough to contribute sig-
nificantly to the N budget of a growing plant community and could
exert a prodigious influence on the long-term behavior of an ecosystem.
Near cattle feedlots where the atmosphere is enriched with feedlot
volatiles, foliar NH3 absorption is probably even higher.  Our data
suggest an important role for green vegetation in the decontamination
of the earth's atmosphere.

A significant amount of the NH3 volatilized from the surface of cattle
feedlots is absorbed by soil and water surfaces in the vicinity of the
feedlots.  The data invalidate the concept that only runoff and deep
percolation from cattle feedlots require control to prevent N enrich-
ment of the surrounding environment.  Although control of runoff into
streams to prevent pollution by sediment, phosphorus, and organic
wastes justifies adequate and often expensive design of feedlot instal-
lations, N pollution can still occur.

There is a potential for aliphatic amines volatilized from feedlots
to affect water ecosystems.  Chemical theory and observations sug-
gest that gaseous aliphatic amines can accumulate in water exposed to
low atmospheric concentrations of these compounds.  Microorganisms

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 that  degrade  aliphatic  amines  were  found  in  lake water.  Microbial
 activity  in water  bodies which absorb  amines is probably sufficient
 to  inhibit amine accumulation  during warm temperature  seasons.  Winter-
 time  accumulation  of  amines may occur  due to the lack  of microbial
 activity  in cold water.

 There is  the  possibility that  individual  aliphatic amines may affect
 the usual spring burst  of algal growth.   Aliphatic amines are toxic to
 Chlovel'la ell-ipeoidea at individual amine concentrations from 1.2 ppm
 for methyl amine to 143 ppm for iso-propyl amine.  The amines appear
 to  stimulate  algal growth at very low  concentrations.  The alga could
 not utilize the amines  as a source of  N,  but amines do accelerate am-
 monium assimilation by  the organism.   Algal  photosynthesis is hindered
 while respiration  is  enhanced  by methyl amine.  The amines may be
 affecting C.  ellipsoidea metabolism by accelerating ammonium assimila-
 tion which would lead to the observed  accelerated consumption of
 oxygen both in the light and in the dark  by  the increased tricarboxy-
 lic acid  cycle consumption of  the oxygen  and would account for the
 lack of decrease in ATP concentration  when methyl amine was added.

 Carbonyl  sulfide and  H2S are produced  from anerobically decomposing
 animal wastes.  Also, observations of  cattle pens and conversations
 with feedlot  operators indicate  substantial  odor reduction when saw-
 dust is generously used as bedding.  In a  related laboratory study,
 adding KNOa to incubating manure eliminated  foul odors.  Thus, promo-
 tion of aerobic processes in feedlot management can reduce odor
problems.  The simplest technique for promoting aerobic conditions is
 to keep the feedlot well drained.

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                              SECTION IV

                           RECOMMENDATIONS


COMPOSITION AND AMOUNT OF RUNOFF INCLUDING RELATION TO CLIMATIC

VARIABLES, SLOPE, STOCKING DENSITY, SITE, SITE MODIFICATION

Pollution control of runoff transport of materials from beef cattle
feedlots can be accomplished best by (1) control of the degree and
length of slope factor utilizing diversions and terraces, (2) use of
debris basins or solids traps to immediately separate readily settle-
able solids from the effluent to eliminate problems of combined storage
of the solids and effluent, and (3) disposal of the solids and the
effluent on cropland after diluting the effluent, if necessary, to
reduce salt concentration.

Weather Factors in Design

It is recommended that the chronic wet periods or periods of continu-
ing wet weather that may be expected over a 10-year period be considered
in designing capacities for feedlot runoff-control systems.

Degree and Length of Slope

In the design of terraces and basins or catchments for sloping beef
cattle feedlots, the degree and length of slope factor should not be
more than three times that normally recommended for cropland in the
eastern Great Plains and Corn Belt.  Long slope lengths increase
solids transport by overland flow and delay drainage.

Terraces and mounds should be employed in beef feedlots to restrict
the length of slope, to improve drainage, and to provide for animal
comfort.  Terraces should not be encumbered by pen fences; this will
permit maintenance and smoothing operations in conjunction with the
removal or mounding of wastes in the feedlot.

Debris Basins

Debris basins in conjunction with feedlot terraces drain better if
constructed in elliptical rather than rectangular shape.  Multiple
riser inlets in a basin should not be spaced further than 40 m
(43.8 yd) apart.  Planned solids accumulation in a basin should not ex-
ceed 20 cm (7.9 inO before removal.  Greater depths require  longer
times to dry adequately for removal and ultimately result in poor
drainage of the basin and odor problems.  In most basins, under eastern
Nebraska conditions, two removals per year will generally be adequate.
Due to variations in storm intensities and amounts and the effects of
                                    8

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 snow and snowmelts, a fixed removal schedule cannot be recommended.
 Experience in eastern Nebraska has shown that required solids removal
 may vary from 1 to 3 times per year.

 Debris basins located within feedlots should not have side slopes
 exceeding 1:4,  and 1:5 is preferable.  Steep slopes,  particularly in
 deep basins,  are subject to increased soil movement,  which is further
 accelerated by cattle traffic.   Steep basin side slopes make removal
 of solids more difficult and during wet weather can become hazards for
 sick or weakened animals.

 Debris basins located outside of feedlots should also be designed to
 permit easy removal of solids.   Again,  the planned depth of solids
 accumulation  should not exceed  the 20-cm (7.9-in.)  depth unless removal
 can be done with a tracklaying  tractor.   Although outside debris  basins
 eliminate some  problems of drainage and solids  accumulation associated
 with basins within the feedlot,  they  introduce  additional areas requir-
 ing maintenance and weed control.   Under some conditions,  flies can
 breed in the  solids collected in outside basins.   This  problem has not
 been observed with basins within the  feedlot.   Crushing of larvae by
 animal traffic  is  a means of insect control.

 Because of the  nature of the runoff from eastern Colorado feedlots,
 debris basin  designs were not evaluated.   Runoff from these lots  is
 very viscous  and similar in physical  characteristics  to the material
 retained in the debris basins in eastern Nebraska.  Thus,  detention
 facilities  in eastern Colorado should be designed  with  primary consid-
 eration for operation as  slurry  storage  and  subsequent  removal of the
 effluent.

 Debris  basins within the  feedlot provide three  advantages:   (1) animal
 traffic hastens  the  drying of nominal depths  of collected  solids;
 C2)  basins  provide protection for  animals  from  wind through much  of
 the  winter; and  (3}  should snow  removal  be required in  the  feedlot,
 basins  are  a  logical  disposal area.

 Solids  Removal

Operators must remember that  a 10-cm  (3.9-in) depth of  dry  organic
material  in a debris  basin or other area within  a  feedlot provides the
 °nly  ingredient required  other than water from  rain or  snow  to create
 a slurry  20 cm  (7.9 in.) or more  in depth.  Removal of accumulated or-
ganic materials  can be accomplished most easily when these materials
are dry  and in nominal depths.

Where debris basins are not used, solids traps utilizing hardware-
cloth screens (9.S cm mesh)  C3.7 in.) in broad,  level channels  are recom-
mended  for separation of readily settleable solids from the runoff.
These solids must be  separated from runoff prior to storage of the

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runoff effluent in a holding pond to reduce production of odors and
eliminate deep accumulations of wet solids which cannot be removed
readily.

Holding Ponds

Sealing of the soil surface after construction of a holding pond should
not be necessary, even on a permeable soil, unless a domestic water
well is located in the immediate vicinity.  The organic solids in the
runoff effluent will soon effectively seal the soil surface to con-
tinued infiltration.

Holding ponds should not be excessively large.  Designs should be for
120 cm (47.2 in.) or greater depths for storage.  Reducing the area
will reduce weed problems and potential salt accumulations.

To reduce odor production, runoff collected during cold or cool
weather should be removed from the holding pond prior to continuing
warm weather.  Holding ponds should be exposed to maximum wind move-
ment.  Feedlots should be constructed downwind from residences and not
in the prevailing wind direction from nearby residences and water bodies,

Drainage Systems

Underground plastic drainlines provide a highly satisfactory means of
discharging runoff effluent from the feedlot or a debris basin.  Flow
may be by gravity or by low pressure from a pump.  Such systems elimi-
nate the problems of settled solids, weed growth, and restrictions of
traffic imposed by open channels.

Corrosion-Resistant Materials
Accelerated erosion due to contact with solids collected from feedlot
runoff or the runoff effluent has not been observed.  Portable aluminum
irrigation pipe and brass sprinkler heads are satisfactory for distri-
bution of effluent.  Galvanized (zinc-coated) hardware cloth and penta-
treated wood can be expected to last for 5 years or more in intermittent
contact with solids collected from runoff.  Pumps with cast-iron or
bronze impellers are satisfactory for pumping the effluent.

DISPOSAL OF RUNOFF

Land Disposal of Runoff

Land application of effluent from feedlot runoff is the most feasible
means of disposal in eastern Nebraska.  Runoff is not a dependable
supply for irrigation, and applications of runoff effluent beyond the
water requirements of crops will be necessary for disposal in wet sea-
sons.  Where irrigation is not practiced, regularly produced field
crops or grass should be grown on the disposal area.

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In the subhumid and semiarid areas, crops with critical-period water
requirements may fail in dry seasons.  Disposal areas twice the size
of the contributing area are adequate in the eastern Great Plains and
in the Com Belt.

The high concentration of solids and salts in runoff from eastern
Colorado precludes its direct application to cropland, unless diluted
with irrigation water to reduce electrical conductivity to a satis-
factory level.

SOIL PROPERTIES UNDER FEEDLOTS

If feedlots are kept stocked continuously, there is little likelihood
that nitrate or other soluble pollutants will percolate through the
soil profile to the water table, even when it is at a very shallow
depth.

Cleaning operations are necessary to remove solid wastes, but scraping
operations should not destroy the interface layer under the manure
layer.

New feedlots should be stocked to capacity immediately and kept at
full capacity at least the first \h years.

INVESTIGATIONS ON METHODS OF EXTRACTION OF NITRATE FROM THE SOIL

PROFILES OF ABANDONED FEEDLOTS

Alfalfa can be established in an abandoned feedlot to prevent or mini-
mize the downward movement of nitrate-nitrogen.  The forage produced is
safe for use for feed.

AIRBORNE POLLUTANTS

Feedlots contribute N to atmosphere principally as NHa but including
amines and other unidentified substances.  Ammonia can be scavenged or
absorbed by plants, soils, and water bodies.  Plants in the vicinity of
feedlots may derive a considerable portion of their nitrogen require-
ment from volatilized ammonia.  Whereas, water bodies may become
eutrophic or well nourished to their N needs.  Since the prevailing
wind is from west to east, it is recommended that, where possible,
feedlots be built windward or east of existing water bodies.  The
toxicity of aliphatic amines to organisms that reside in the vicinity
of cattle feedlots does not appear to be an immediately acute problem.
The potential does exist for direct ill effects on organisms in an
area to occur as the cattle population density increases.  The synthesis
of aliphatic amines, carbonyl sulfide, and H2S is engendered by anaero-
bic conditions in the feedlot manure pack.  For feedlot odor control,
it is important that the feedlot be kept as well drained as possible.


                                   11

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Management practices, such as using sawdust mulches, which keep the
manure pack as aerobic as possible should keep the production of
aliphatic amine, carbonyl sulfide, and H2S to a minimum.
                                    12

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                                SECTION V

      DESCRIPTIONS  OF FIELD SITES,  SPECIAL  FACILITIES, AND METHODS


NEBRASKA SITES

Level Feedlot,  Central  City,  Nebraska

A level  feedlot has  been under  study in the Platte  River valley  on  the
T. C.  Reeves' farm,  west of Central City in Merrick County,  about 165
km  (102 miles) west of Lincoln.   The  soil is  a  silt loam underlain
with  sand and gravel and a water table  that fluctuates between 60 and
305 cm (23.6 and 120 in.).   The  water table is  lowered during irriga-
tion  and recovers  rapidly  following heavy rainfall.  Groundwater levels,
movement,  and quality were measured (2,  3, 4).

Caissons  were installed to a  depth of  183 cm  (72 in} beneath the feed-
lot surface so  pollutants  in  the soil water and gases in the soil
profile  could be studied.   The  caissons  contained portholes  so soil-
solution and soil-gas samplers  could be  placed at increments in  the
soil  profile.   In  this  manner,  in  situ  samples could be obtained from
the same  point  over  long time periods.   Soil-solution samples were
used  to  assess  pollutants  moving through the soil profile and soil-gas
samples  were used  to determine  the reduction status of the soil  profile.
A caisson prior to installation is shown in Figure  1 and an  installed
caisson  with samplers in place  is  shown  in Figure 2.  Caisson design,
installation, and  sampling equipment are described  in detail by  Elli-
ott,  McCalla, Swanson,  and Viets (5).

Manure accumulated on this  lot  without  appreciable  removal for 15
years.  The manure pack was 30  to  40 cm  (11-8 to 15.7 in.) deep when
mounds were first built in August  1969.  In late 1971, a moderate
slope was built into drainways  between the three mounds in the lot,
with  drainage to three  sumps  connected by underground lines.  Runoff
collects  in the central sump  and is pumped underground to a  holding
pond  lined with polyethylene.   This system has functioned well since
installation.   Lack  of  drainage during wet weather has presented
severe problems on this lot in  the past  (6).

Traps containing dilute sulfuric acid were used on this site to  com-
pare  the NH3 contents of the  air in the immediate vicinity of the
feedlot with air in  surrounding cropland and to identify odor
compounds  (7).

Sloping Peedlot on Deep Loess Hill, Gretna, Nebraska

A sloping feedlot with a southern  exposure on a typical, deep loess
hill is being studied on the Howard Krambeck farm,  north of Gretna in

                                    13

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Figure 1.   Caisson before installation in the  soil

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Figure 2.  Installed suction cup assemblies and gas samplers.

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western Sarpy County.  Runoff from rain and snow and the movement of
organic wastes and soil were measured.  Climatic factors, in addition
to rainfall, were measured to evaluate their effects on the amount of
runoff and solids transported.  Solar radiation, evaporation, wind
movement and direction, soil water under the feedlot and adjacent
grassland, as well as groundwater quality and water levels were meas-
ured.  A trap was installed to collect solids transported in the runoff
prior to their reaching the holding pond.  A programmed, automated
sampler was used to monitor runoff quality (8).

The solids trap consisting of three, hardware-cloth screens set across
a 4.3- by 26-m (1.7- to 10.2-in.) channel retained most of the solids
before the runoff reached the holding pond.  The debris trap was
cleaned periodically with a tractor-mounted, front-end loader (9).

Steep, Sloping Feedlot with a Broad-basin Terrace, Omaha, Nebraska

Broad-basin terraces have proved to be a workable method of feedlot
runoff control.  A broad-basin terrace was installed on a lot with a
15% easterly slope at Underwood Farms, northwest of Omaha.  The runoff
plus solids was collected in the basin.  Recorders in the basin meas-
ured the amount and rate of runoff inflow.  The runoff water was pumped
from the basin and applied to adjacent cropland.  The solids drained
and dried sufficiently for removal with a front-end loader.  The basin
had a capacity of 30 cm (11.8 in.) of runoff and did not have to be
emptied frequently (10).

Sloping Feedlot with Broad-basin Terraces, Springfield, Nebraska

Broad-basin terraces were installed on a feedlot with a southwesterly
7% slope, 183 m (200 yd) long, west of Springfield at the William
Cockerill farm.  Each terrace retains runoff from an area of a differ-
ent size.  This installation was equipped with runoff-recording equip-
ment, and underground plastic pipe drained the water from the terrace
basins to storage in a holding pond from which it was pumped for
application on cropland (10).   Physical and chemical effects of runoff-
effluent applications on the soil and plants from Ladino clover, tall
fescue, perennial ryegrass, corn, and forage sorghum plots were
studied.   Yields and nutrient content of the crops were measured.
Three caissons were installed on this site (one on the slope, one in a
basin of the feedlot, and one in an adjacent field) to monitor pollu-
tants in the soil water and gases in the soil profile to determine what
occurs under a newly established feedlot.

The terrace system on this feedlot was altered in 1973 to provide better
cattle access to feedbunks and waterers.   Pen fences were moved from the
terrace crowns and riser inlets were installed near the center of the
debris basins.   The outlet from the lower basin was moved from the
                                    16

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 holding pond  and  extended  to  discharge  onto  a  leveled  area  of  cropland.
 The  cropland  area was  surrounded by  a low  earthern  dike to  prevent
 runoff.

 Feedlot Located on Streambank, Coifax County, Nebraska

 This site on  the  William Krula farm was located partially on the flood-
 plain of East Fork of Maple Creek, which has a long history of serious
 flooding.  The installation included a dike, 3 m  (3.3  yd) high, built
 along the lower side of the feedlot.  The top of the dike was 60 cm
 (23.6 in.) above the record flood stage and kept feedlot runoff and
 wastes out of Maple Creek during any storm.  The basin in the feedlot
 was about 150 m (164 yd) long and 15 m (16.4 yd) wide  at the bottom,
 with 4:1 slopes coming into it.  The basin held 10 cm  (3.9 in.)  of run-
 off plus 1.3 cm (0.5 in) of solids from the 2.63 ha.(6.5 acres)
 drained in this portion of the lot.   This is adequate capacity for any
 24-hour storm expected in a 10-year period (11).

 Runoff from the feedlot collected in the basin and drained through
 three riser inlets,  then through a 15-cm (5.9 in)  plastic underground
 line into a sump equipped with a 1/2 hp  electric sump pump.   The runoff
 was pumped through a 7.6-cm (3-in) plastic line to a holding pond near
 the lot on a higher  elevation.  The  runoff collected in the  holding
 pond was  spread as irrigation  water  on  an irrigated  field near  the
 holding pond.   This  water spreading  was  done  during  dry weather,  util-
 izing a large, plastic  siphon  connected  to  gated  irrigation  pipe.

 This  feedlot  also  included  a broad-basin terrace with an underground
 pipe  discharge to  the holding  pond and has  capacity  for about 1,000
 cattle.

 Feedlot with a Defined  Drainage Channel, Stanton County, Nebraska

 This  installation  included  a series of lots or pens  on  the Paul Wiemann
 arm  traversed by  continuing drainway.  Runoff from outside the
 leecuot site was diverted by means of a diversion terrace.  Wooden
 frames, covered with hardware-cloth screens, served  as  debris traps
 and are located at selected locations in the drainway through the lots.
 Upon  leaving the lots, the drainway entered a nearly level,  12- by
 120-m (13 by 131 in.) debris trap, similarly equipped with such screens.
 The runoff deppsted most of its solids before discharging into a drop
i^let to a holding pond for later application to an adjacent field.
This site also included a lot with a broad-basin terrace with an under-
ground discharged  to the holding pond.  The total capacity was in
excess of 1,000 cattle.
                                    17

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 Beef Cattle Feeding Complex, University of Nebraska Field Laboratory,
  Mead, Nebraska

Specially constructed pairs of pens with 3%, 6%, and 9% slopes have been
studied at the University of Nebraska Field Laboratory.  Detention ba-
sins were constructed at the lower end of each lot to retain runoff.
Each basin was equipped with a water-level recorder to record the dura-
tion, rate, and quantity of runoff.  Two stocking rates were studied
simultaneously in the pairs of pens to learn the effects of animal den-
sity and surface slope on characteristics of runoff, solid wastes, and
nitrate movement on unpaved, beef feedlots.

Two systems of runoff control also have been studied at this site to
determine the pollutants and solids transported from the feedlot pens.
One system collected the runoff and solids from a runoff event; the
effluent was drained off after the solids settled.  The second system
utilized rock-filled dams in a nearly level channel to retain the
solids and permit drainage of the runoff effluent to a holding pond.

Abandoned Feedlot Study, Gretna, Nebraska

To study the pollution potential of abandoned feedlots, an active feed-
lot was selected and a portion of it abandoned.  The site, on the
Rodney Weeth farm, was on an upland slope on typical, deep loess soil,
just south of Gretna, in western Sarpy County,  The area is being
cropped with alfalfa  and corn to remove nitrogen from the soil pro-
file and to attempt prevention of downward movement of nitrate.

Core Drilling Study of Nebraska Beef Cattle Feedlots

Fifteen feedlot sites in four eastern Nebraska counties were selected
for this study.  The sites were located in Cuming, Douglas, Sarpy,
and Polk counties, where large numbers of cattle are fed in confined
feedlots.  One or more sites were used to evaluate each of the effects
of feedlot age, management, soil texture, and topography on the nu-
trient status of the soil profile and groundwater.  Six feedlots were
located in the Elkhorn River Basin, five in the Platte River Basin, and
four in the Papio Creek Basin.  Two of the Platte River Basin sites
were on the floodplain.  One hundred and three cores were taken from
feedlots, 22 from cropland, and 4 from cropland-cattle-use areas.

Management considerations included stocking rate, manure-scraping, and
mounding practices.  Age of feedlots sampled ranged from a few
weeks to more than 50 years, with the soil textures ranging from clay
to coarse sand.  Cropland and grassland areas were cored adjacent to
feedlots for comparisons.

Soil samples were taken with a mobdle, truck-mounted, coring rig.  On
most core locations, 5.1-cm C2-inJ diameter, 122-cm (48-in} long cores

                                    18

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 were taken through the profile, using hydraulic pressure.  In dense
 and sandy soils, a driving hammer and a 3.5-cm  (1 3/8-in} split-tube
 sampler were used.  Each core was divided into 30.5-cm  (12-in}
 sections.  Alternate sections were placed in a plastic bag, sealed,
 and frozen immediately with dry ice.  These samples remained frozen
 until chemical analyses were performed.  The other sections of the
 core were placed in a bag and retained for physical determinations.
 Percent moisture by weight (Pw) was determined on each sample.  Soil
 texture was estimated by feel at the sample site; where there was a
 sharp textural change, samples were taken from above and below the
 transition.   Random comparisons were made of the texture estimates
 made in the field with those obtained by the standard hydrometer
 method.

 Oxidation reduction potential (Eh)  measurements were taken immediately
 after cores  were removed from the sampling tube.   A platinum and refer-
 ence electrode was  pushed into the  sample,  and the reading taken 60
 seconds  later was corrected to the  standard hydrogen electrode.

 If groundwater was  reached,  water samples  were obtained.   A small,
 hand-vacuum  pump was  used whenever  possible; however,  on deeper  sam-
 ples  a  tube  sampler 60 cm (23.6 inO  long with check  valve was  used.
 Some  water samples  were obtained by pouring off the  water trapped  in
 the sampler  above the  soil  core.

 Specific profiles were  selected from which  samples were  chosen to
 characterize  the bulk  density and the percent water  at  I/10-,  1/3-,
 and 15-bar suctions by  standard procedures.   The  clod method was used
 to determine  bulk density.

 COLORADO SITES

 Level Feedlot  CAnderson)  and  Sloping  feedlot (Ashlind), Ft. Collins,
   Colorado

 Two commercial  feedlot sites near Fort Collins were selected for hy-
 drologic evaluation.  The flat site  (Anderson) is on very permeable
 s°il immediately  adjacent to the Cache la Poudre River, about 5 km
 (3  miles) east  of Ft. Collins, and was selected for its potential
 for groundwater pollution.  The second (Ashlind) site, about 7.5 km
 (4.5 miles) northeast of Ft. Collins, is constructed on a deep, fine-
 textured soil with a uniform slope of 6% and represents a typical
 feedlot for the area having potential for surface water pollution.

The flat feedlot  is 0.2 ha.(.5 acre) in size and is normally stocked
with 70 head of cattle.  A climatic station, including standard and
recording rain gages, anemometer, hygrothermograph, standard class A
evaporation pan, and maximum and minimum thermometers, was installed
near this feedlot.  Three vacuum lysimeters  (12) (see Figure 3) were

                                  19

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Figure 3.   Vacuum lysimeter ready to be lowered into position
                near center of flat (Anderson)  feedlot.
                                  20

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 installed to determine the quantity and quality of percolate moving
 through the soil profile.  One lysimeter was installed immediately
 behind the concrete feedbunk apron where the soil was continually
 moist from animal excretion.  A second lysimeter was placed in the
 normally dry center of the lot, with the third at an intermediate
 position.  The cobble subsoil precluded installation of access tubes
 for neutron soil water measurements.

 During the years 1969 and 1970, the animal drinking water was measured
 directly with a domestic water meter, but then a change in water source
 and attendant trash problems rendered the meter inoperative.  Subse-
 quent drinking water consumption was calculated from the number of
 animals in the lot and earlier measured consumption for a comparable
 time of year.

 The sloping (Ashlind)  lot covers 0.4 ha. (1 acre)  and is normally
 stocked with about 225 head of cattle.   This site was equipped with
 three vacuum lysimeters as in the flat  lot.   After 2 years of opera-
 tion, no detectable movement of percolate had been measured, and
 further operation of the lysimeters was discontinued.  Six tubes for
 neutron measurement of soil water were  located randomly through the
 lot to further delineate changes in soil  water content.   A diversion
 dike constructed near  the lower end of  the lot (Figure 4)  diverted
 surface runoff through a recorder-equipped flume  for quantitative
 measurement.   A pump sampler was provided to collect periodic sam-
 ples during each runoff event.   However,  as  apparent from Figure 4,
 the surface water leaving the feedlot during a runoff event was very
 heavily sediment laden.   This heavy sediment concentration made it
 impossible  to  collect  samples by pumping;  therefore,  only periodic
 grab samples were available for chemical  analysis.

 Because  of  the  proximity  of the two sites  (5.8 km or 3.6 miles),  only
 the standard and recording rain gages were installed for  climato-
 logical measurements at  the Ashlind site.

 Caissons at Ashlind  Feeders,  Inc.

 A nearly level  feedlot pen located  downslope  from the vacuum lysimeter
 installation at Ashlind Feeders,  Inc.,  along  with a nearby alfalfa
 field, was selected in December,  1970,  for installation of three
 steel-cased caissons similar  to those already described.   One caisson
 was  instal-led near the feedbunk, the lowest elevation in the pen, and
 the  other near  the center  at  the highest elevation.  The third  cais-
 son  in the nearby alfalfa  field served  as cropped field comparison.
 The  caissons were instrumented in 1971  to collect data on  soil  tem-
peratures, soil water tension, soil gases, and soil solutions.  All
 three caissons were placed deep enough  to reach the water  table or
well within the capillary  fringe of the water table, 3.7 to 4.3
meters (12 to 14.1 ft).

                                 21

-------
Figure 4.   Sloping (Ashlind)  feedlot immediately following 6.6 cm
           of rainfall, June 1970.   Note diversion dike in left
           center of photo and extremely viscous liquid draining
           toward flume in immediate foreground.
                                  22

-------
 Experimental Percolation Feedlot,  Colorado State University,  Fort
   Collins

 Observations of the Ashlind and Anderson feedlots led to  the  develop-
 ment in late 1971 of plans for a major research facility  for  evaluating
 effects of feedlot management on percolation of pollutants.   It  was
 hypothesized that manure pack management could reduce the quantity and
 concentration of pollutants in percolating soil water.  To test  the
 hypothesis,  a research feedlot was constructed at the Colorado State
 University Animal Research Center, 7.5 km (4.7 miles)  southeast  of Ft.
 Collins.   The research feedlot, with  30-head capacity,  is 15.2 by 22.9
 meters  (16.6 yd by 25 yd)  in area. Two underground  tunnels were con-
 structed,  one under the feeding apron, the second near the center of
 the  lot,  to  provide access to the  soil profile beneath the feedlot.
 Figure  5  illustrates the tunnel under the feeding apron during con-
 struction.

 Eight artificial soil profiles have been constructed downslope from
 each of the  two tunnels.   Each of  these profiles  was placed in a pit,
 1.2m by  2.4m by 1.8m deep (3.9  ft  by 7.9 ft by 5.9  ft), excavated
 adjacent  to  the tunnels.   These pits  were  lined with a continuous
 sheet of  butyl  rubber to assure capture of all percolating water.
 Each pit  is  provided with  gravity  drains,  which allow maintenance of
 the  water  table at any depth to 183 cm (72.1  in}  below  the soil  sur-
 face.   Porous  ceramic drains are also provided to allow removal  of
 percolate  at sub-atmospheric pressure,  thereby simulating a water
 table depth  down to 7.6 m  (24.9 ft).

 Four soil profiles  replicated four times are  shown in Figure 6.  The
 plots upslope  from Unit  B  have  not been installed although access
 holes have been provided through the  tunnel walls to allow future in-
 stallation of  these additional  plots.   The  uniform sand profile will
 be sufficiently aerated  to maintain aerobic conditions throughout.
 The  clay  loam will  be  irrigated if necessary  to maintain  an anaerobic
 profile.  The clay/sand profile  is intended to maintain the upper
 layer anaerobic and the  deeper  layer  aerobic.   The sand/clay profile
 is intended  to  provide nitrification  in the upper aerobic  layer with
 subsequent denitrification as water moves into  the anaerobic zone
beneath.

Each of these test plots is provided with either  gravity or vacuum
drainage to provide the degree of  aeration mentioned above.  Tensio-
meters throughout the profile will be used to  indicate soil water
status  (thereby  inferring  degree of aeration).  Gas  and water samples
 collected at various depths will be analyzed to determine the chemical
changes as the water moves through the profile.
                                23

-------
Figure 5.   Access tunnel, experimental feedlot, prior to
              backfill and completion of feeding apron.
                                   24

-------
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                               25

-------
                                SECTION VI

        COMPOSITION  AND  AMOUNT  OF  RUNOFF  INCLUDING  RELATION  TO

 CLIMATIC  VARIABLES,  SLOPE,  STOCKING  DENSITY,  SITE,  SITE MODIFICATION


 NEBRASKA

 Amount  of Runoff

 The  feedlot  at Gretna has a single pen isolated  for runoff  measurement.
 This pen, approximately 37  m 0*0.5 yd) wide with a 91-m  (100 /d)  slope
 length  and a 6% slope,  has  a southern exposure.  From July, 1968,
 through December, 1972,  precipitation totaled 314  cm (123.7 in} and
 occurred  on  323 days.   There were 89 runoff events  and 104  cm  (113.8
 in,)  of  runoff  (Table 1).  It is estimated that about 23 cm  (9.1 in)
 of runoff can be expected annually from  a sloping  feedlot with 71 cm
 (28  in} of average  annual precipitation  (13).

 A programmed sampler, which passes a slotted  dipper through the runoff
 discharge, is used  at this  site.  Discrete samples  of the runoff and
 its  bedload  are obtained over  5-minute periods.  The sampler is pro-
 grammed to select 14 samples at preselected times  during runoff.
 This permits both qualitative  and quantitative evaluation of the
 runoff  with  elapsed time (8),


 Table 1.  SUMMARY OF RUNOFF EVENTS FROM  FEEDLOT  PEN, GRETNA, NEBRASKA,

                               1968-1972

Year
1968a
1969
1970
1971
1972

Days with
precipitation
29
81
72
62
79

Runoff
events
12
20
23
15
19
Total
precipitation
(cm)
49.93
56.13
61.90
67.49
76.66

Runoff
(cm)
22.17
14.45
14.22
23.29
29.92
Total        323              89         312.11            104.06

o
 Incomplete record for year; record started with runoff event
 on July 17.


                                    26

-------
 The data obtained show that runoff may not be expected from rainfall
 °f 1.3 cm (.51 in.) or less unless rainfall has occurred within the
 previous 72 hours.  These data also show that higher rainfall inten-
 sities provide both higher runoff rates and increased total runoff.
 Water storage in the soil and manure mixture on the feedlot surface
 can be appreciable.  However, appreciable water movement into the
 soil profile of a feedlot with an established manure pack should not
 be expected during, or from, a rainfall event.  Profile moisture
 measurements show that wetting of the feedlot surface is relatively
 slow, but significant amounts of rainfall are stored in the organic
 surface.   The stored water is usually lost to evaporation soon after
 the rain.

 Runoff amounts from rains received within one day after other runoff-
 producing events did not approach rainfall amounts except for rela-
 tively high-intensity rains.   A regression analysis was made of
 runoff from 19 individual storms that followed runoff-producing rains.
 The resulting equation was:   runoff = 0.03 + 1.04 x rainfall,  with a
 correlation coefficient of 0.78.   This suggests  that once moistened,
 the feedlot surface absorbs  water more rapidly.

 Pollutants  Transported in Runoff

 A  selected  hydrograph with the runoff-site  relationships  for runoff
 fyom  the April  18,  1970,  event CFig.  7)  shows  that the  comparatively
 high  initial  NH^-N  and N03-N  contents  drop  rapidly (.23  to 9  ppm and
 9  to  l  ppm>  respectively)  during the  first  hour  after runoff starts.
 This  occurred with  a continuing rainfall  intensity of about  0.5 cm/hr.
 A  similar hydrograph for  the  following day  (Fig.  8)  indicates  that
 after a short cessation of rainfall,  the  NHi+-N content  of the  runoff
 again will be relatively  high  (16 ppm)  and  may be  expected to  drop
 (2 Ppm) within  an hour.   On the  other  hand,  the N03-N content  (less
 than  l ppm) vm not  increase  with the  resumption  of runoff.   The
 NIVN and N03-N are washed out rapidly  from the feedlot surface by the
 runoff.  However, only a  short interval without runoff  is  required for
 the accumulation of additional NH^-N for  subsequent  removal.

A similar relationship is  shown by N03-N  in  the runoff  for the Sep-
 tember  23, 1970, storm  (Fig. 9) except  that NHi+-N  in  the  runoff
 fluctuated  (27 to 12 ppm)  throughout the  5.5-hour  sampling period.
    total solids content in runoff that occurred on April 18 and 19,
1970, ranged from 0.40% to 1.52% and from 0.46 % to 1.26%, respec-
tively.  The September 23 runoff had a solids content ranging from
°-36% to 0.54%.  The higher solids contents observed during the
APril 18-19 runoff events occurrred in conjunction with periods of
higher rainfall intensity, although the intensities ranged only from
°-5 to 0.65 cm/hr (..2 to .26 in/hr) .  Even very moderate increases in
rainfall intensities can be expected to greatly increase the solids

-------
KJ
00
                   2.5
                 62.0
                 o
0  1
Z  L
D

-------
K>
                       F
                  o
                  z
                  D
                  £0.5-
                  <
                  CC.
                               100    200   300     400

                                            TIME ,   min
                                                                               1(6
                  0
500   600    700
           Figure 8.   Rainfall, runoff,  and NH^-N and N03-N concentrations in runoff, sloping

                                cattle  feedlot, Gretna, Nebraska, April 19, 1970.

-------
u>
o
                                 100
200       300

  TIME,  min
400
                                                                                125
                                                                                      a
                                                                                      a
500
            Figure 9.  Rainfall, runoff, and NH^-N  and N03-N concentrations in runoff,  sloping

                              cattle feedlot,  Gretna, Nebraska,  September 23, 1970.

-------
 transport from a sloping  feedlot by a unit depth or volume of water.
 This effect is significant because a 1% solids  content in runoff is
 equivalent to 10 metric tons of solids in a  10-cm depth over a
 hectare  (4.46 tons/acre).

 Based on the data presented, 30.48 cm (12 in} of feedlot runoff may
 contain from 27 to 2.5 kg (59.5 to 5.5 Ibs)  of NHit-N, from 10 to less
 than 1 kg (22 to 2.2 Ibs) of N03-N, and about 45 kg (99 Ibs) of P.
 From April through October, 1970, a total of 91 runoff samples were
 analyzed from 10 storms, providing three or  more samples per storm.
 The chemical oxygen demand ranged from 144 to 12,790 ppm.  Phosphorus
 ranged from 0 to 771 ppm and averaged 38.8 ppm.  Solids ranged from
 0.18% to 2.18% with an average of 0.75%.   Volatile solids ranged from
 19.6% to 75.0% of the total solids and averaged 36.0%.  Assuming that
 the average solids content of runoff from the feedlot will not exceed
 1% for an expected 23 cm (9.1 in)  annual  runoff, the annual solids
 loss can be estimated at 23 metric tons per hectare (10.3 tons/acre),

 A solids trap,  consisting of a broad,  flat channel  4.3 m (4.7 yd)
 wide and 26 m (28.4 yd) long with three transverse  screens,  was  in-
 stalled to collect solids from runoff of  the feedlot at Gretna.   A
 total of 78 m3 (.76 acre-inches)  of solids were retained in the  trap
 from July,  1969,  through February,  1971.   Bulk densities of these
 solids  ranged from 0.36 to 0.66 g/cm3 (.013 to .024 Ib/cubic inch).
 Rainfall totaling 101.1 cm (39.8  inO  for  the 39 runoff events during
 the 2%  -year  period contributed to  39.6 cm (15.6 in)  of runoff,  which
 deposited an  estimated  38.8  metric  tons  (42.8 tons)  of solids in the
 trap.   Total  precipitation for the  2^- year interval  was  159  cm (62.6
 int).  The trap has  an estimated efficiency of 80% for settleable
 solids.   The  solids retained by the trap  ranged  from 22%  to  59%
 organic  matter at  the time of removal  (9).

 It  also  can be estimated further that soil  and organic matter equiva-
 lent  to  2.4 cm on the feedlot was carried  in  the 101.1 cm of  runoff.
 If  a  bulk density of  0.50  is  assumed, the  average solids  content of
    runoff was 1.2%.
Solids Transport

Solids transport by runoff was measured  also by solids accumulations
removed from basins of  feedlot terraces  at Omaha and Springfield.
These values are shown  in Table 2.  The  solids movement on all three
sites falls into the expected pattern for slope and slope length  (10)

       and Pollutants
At Mead, as well as at Springfield, Nebraska, about 23 cm  (9 in) of
the 71 cm (28 in; annual precipitation will run off (14).  Three to
six percent of the material deposited on a feedlot will be transported
*n the rainfall runoff.  The quantity of material removed will be much
higher if snowmelt runoff is included.
                                   31

-------
        Table 2.   SOLIDS ACCUMULATIONS  REMOVED FROM BASINS  OF FEEDLOT TERRACES  WITH  CONTRIBUTING  AREAS



                     OF VARYING SLOPE AND SLOPE LENGTHS,  OMAHA AND SPRINGFIELD,  NEBRASKA, JULY  1971
u
to
*
Location \ Slope,
Omaha 15
Springfield
Basin- 1 5
Basin-2 6
Basin-3 7
; slope ;
; length, ;
104

30.5
45.7
51.8
Basin
area
(m2)
1,300

697
1,104
641
; so lids a;
volume
: (m3) :
15,115

2,519
2,408
3,229
Equivalent
depth in
basin
(cm)
43

13.4
8.2
18.6
\ Contrib-
uting
area
; (m2)
5,472

1,623
4,180
5,149
:Total '
; lot ;
area
I Cm2) !
6,772

2,320
5,283
5,790
Equivalent
depth in
lot
(cm)
8.26

4.02
1.68
2.07
          Total accumulation since construction in July 1969.

-------
 The characteristics and chemical composition of runoff from snowmelt
 and rain are shown in Table 3.  The annual quantities of materials
 removed in runoff from feedlots in rainstorms and during snowmelt run-
 off are shown in Table 4.  The pH ranged from 4.0 to 9.4, and elec-
 trical conductivity was as high as 4.9 and 19.8 mmhos/cm in summer and
 snowmelt runoff, respectively.  Percent total solids were lower in the
 runoff from rainstorms than from snowmelt.  When thaws occurred during
 some winters, a slurry of undecomposed manure flowed from the lot.
 The snowmelt runoff that contained high solids content occurred only
 from lots with cattle that we on high-concentrate diets.   Total N in
 the winter runoff was as high as 6,500 ppm.  Nitrate-N varied from 0
 to 280 ppm in the runoff from rain.

 In 1969,  an appreciable amount of material was removed in the snowmelt —
 119 and 26.9 metric ton/ha, (S3 and 12 tons/acre)  for 9.3  and 18. 62/
 animal densities, respectively.   Approximately half of the material was
 yolatile  solids.  Significant amounts of P and N  also left the feedlot
 xn runoff.   The  runoff varied from year to year.   Two to  three times
 as much material was  removed from the 9.3 m2/animal (100  sq ft/ animal)
 lot as from the  18.62/animal (200 sq  ft/animal)  lot for 1969 and  1970.

 Chemical  element content  of the  runoff is shown in Table  5.   Potassium
 and Mg were high.


 COLORADO

 Composition and  Amount  of  Runoff

 Since  the flat (Anderson)  feedlot has  no  external  drainage,  surface
 runoff Was  not a consideration at that site during this study.  At the
 sloping (Ashlind) site, runoff resulted from only  four to seven rain-
 fall events  each  year.  Figure 10 shows the relation between runoff-
producing precipitation and  the  depth  of  runoff produced.  The correla-
tion between rainfall and runoff was highest when  the precipitation
during  a 72-hour period was used for correlation.  Accumulation of
rainfall over a  72-hour period apparently compensates for the antece-
dent moisture in the manure pack.  It  appears that the water-holding
capacity of the manure pack is relatively constant, so long as a
manure pack is present.  Runoff was never observed during a 72-hour
storm of less than 1 cm (0.4 inch), and every storm exceeding that
amount produced measurable runoff.
    annual precipitation and runoff at the Ashlind site during the
study period is summarized in Table 6.

Prom Table 1, it is apparent that 15.5 percent of the total precipi-
tation left the feedlot as surface runoff.  However, as seen in Fig.
10*  about 40% of the precipitation from any event exceeding 1 cm
                                    33

-------
Table 3.  RANGES IN THE CHARACTERISTICS AND CHEMICAL VALUES OF RUNOFF
             FROM BEEF CATTLE FEEDLOTS, MEAD, NEBRASKA, 1968-1972
Snowmelt runoff

pH
Conductivity (mmhos/cm)
Total solids (%)
Volatile solids (%)
Ash (%)
COD (mg/1)
P (ppm)
NH4-N (ppm)
N03-N (ppm)
Total nitrogen (ppm)
Low
4.1
3.0
0.8
0.6
0.2
14,100
5
6.0
0
190
High
9.0
19.8
21.8
14.3
9.2
77,100
917
2,028
280
6,528
Mean
6.3
7.1
7.7
3.9
3.8
41,000
292
780
17.5
2,105
Rainstorm runoff
Low
4.8
0.9
0.24
0.12
0.12
1,300
4
2
0
11
High
9.4
5.3
3.3
1.5
2.8
8,200
5,200
1,425
217
8,593
Mean
7.0
3.2
1.93
0.82
1.11
3,100
300
151
10
854

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    Table 4.  QUANTITY OF MATERIALS  REMOVED IN RUNOFF FROM BEEF CATTLE

                        FEEDLOT, MEAD, NEBRASKA,  1969-1972



1969
Precipitation (cm)
Runoff (cm)
Total solids (Mt/ha)
volatile solids (Mt/ha.)
Ash (Mt/ha,)
Total N (Mt/ha.
1970_
Precipitation (cm)
Runoff (cm)
Total solids (Mt/ha.)
Volatile solids "
^h (Mt/ha.)
Total N (Mt/ha.)
Total P (Mt/ha.)
Precipitation (cm)
R^off (cm)
rotal solids (Mt/ha.)
volatile solids (Mt/ha^
Total
Jan 1
9.3



36.10a
17.10
134.00
69.50
64.90
3.83

36.80
14.70
56.10
33.20
22.90
0.21
0.30



year
Dec 1
18.6



36.10
16.60
42.60
21.20
21.40
1.26

36.80
19.30
38.20
20.50
17.70
1.44
0.23
42.60
24.60
53.50
19.10
Snowmelt
Jan 1
9.3
- m2 per

8.39
6.76
119.00
62.60
56.80
3.16

2.98
1.58
2.09
1.55
0.47
0.21
0.01



Apr 4
18.6
animal —

8.39
4.55
28.00
14.30
13.70
0.88

2.98
2.01
1.28
0.88
0.41
0,74
0.12



Rainstorm
Apr 5
9.3



27.70
10.30
15.00
6.90
8,07
0.68

33.80
13.10
54.00
31.60
22.40
1.80
0.27



Dec 31
18.6



27.70
12.00
14.50
6.81
7.69
0.38

33.80
17.30
37.00
19.60
17.30
0.70
0.14
42.60
24.60
53.50
19.10
£sft (Mt/ha.)                       34.40
Total N (Mt/ha.)                    1.39
Total P (Mt/ha.                    0.32
1972

frecipitati
*unoff (cm)
Total solids ^
Volatile solids
Ash (Mt/ha}
Total N (Mt/ha.)
r°tal p (Mt/ha)
  Precipitation causing a runoff event
34.40
 1.39
 0.32
an (cm)

3 (Mt/ha.)
Lids "

/ha.)
/ha)
38.30
25.30
64.80
28.10
36.70
2.18
0.14
38.30
25.30
64.80
28.10
36.70
2.18
0.14
                                     35

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                   2345
                      72 HR.  PRECIPITATION, cm
6
Figure 10.  Precipitation-runoff relationship for sloping CAshlind)  feedlot.

-------
             Table 5.  CHEMICAL ELEMENTS IN RUNOFF FROM BEEF

                           CATTLE FEEDLOTS, MEAD NEBRASKA
Chemical

Na
K
Ca
Mg
Zn
Cu
Fe
Mn
Concentration range
Low


90
50
75
30
1
0.6
24
0.5
High

ppm
2750
8250
3460
2350
415
28
4170
146
Mean


840
2519
794
494
107
7.6
764
26.7
          Table 6.  ANNUAL PRECIPITATION AND RUNOFF - ASHLIND
                                     (cm)
Year
1970
1971
1972
Precipitation
28.09
29.10
27.30
Runoff
5.66
7.40
.09
 (•39  in)  ran  off the  surface.  Hydrologic  studies  at both  sites were
terminated at the end of  calendar year  1972.

Table  7 shows the composition of runoff from feedlots near Fort Collins
Colorado.  The low annual precipitation and infrequent storms are
reflected in the high total solids content of runoff from  the sloping
Ashlind site (20.4% total solids) compared to that of Mead, Nebraska,
in Table 5, which had an  average content of 2.0%.  In fact, the
                                   37

-------
composition of rainfall runoff at Ft. Collins compares with snowmelt
runoff at Mead, Nebraska.  Concentration of the chemical species for
runoff showed higher values for total, suspended and dissolved solids,
NOs, NHij, and total N for material from the sloping lot  (facing to the
south) than for the level lot in an arid area.  In addition, the
runoff from Colorado feedlots is higher in salts as is shown by an
electrical conductivity of 8 to 12 mmhos/cm as compared  to rainfall
runoff at Mead, Nebraska, of 0.9 to 4.9 mmhos/cm.
       Table 7.  CHEMICAL COMPOSITION OF RUNOFF FROM FEEDLOTS

                            NEAR FORT COLLINS, COLORADO
Measurement
                                          Feedlot - Slope
unit
Total solids (g/1)
Suspended solids (g/1
Dissolved solids (g/1)
EC (mmhos/cm at 25°C)
PH
NO 3 (ppm)
N02" (ppm)
NHj,. (ppm)
N (total, ppm)
POif (ppm)
P (total, ppm)
COD (mg 02/1)
Anderson - 0%
17.5
11.8
6.6
8.59
7.19
2.96
0.0
358.0
1,153.5
114.0
92.5
17,800.0
Ashlind - 6% -8%
204.0
195.6
8.4
12.80
6.75
43.4
0.0
1,130.0
7,370.0



                                   38

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                                 SECTION VII

                             DISPOSAL OF RUNOFF


  NEBRASKA CONDITIONS

  As previously stated,  land application for crop utilization of the
  effluent from feedlot  runoff is the most feasible means  of disposal
  under Nebraska conditions  and in most of the United  States.   In addi-
  tion to the studies discussed,  with crops of grass,  Ladino clover, corn,
  and forage sorghum at  Springfield,  effluent has been applied to brome-
  grass at Gretna and to cropland used for producing ensilage  at  Omaha.

  At Gretna,  established, pastured brome  has  been subjected  to applica-
  tions of effluent  at various  times  during the season, using  both
  surface  flow  and sprinkler application.   The times of application have
  been  random,  dependent upon preceding runoff events.  Continued obser-
  vation has  not  indicated other  than  generally beneficial effects from
  the effluent  applications.  No  evidence of  selective  grazing  (that is,
  avoidance by  the cattle of areas  on which the effluent was applied)  was
 noted.   Increased forage production  and plant vigor were noted.

 Effluent applications at the Omaha site have also been dependent upon
 previous runoff events and have been made by sprinkler and surface
 application.  Forage sorghum stands were not changed by effluent appli-
 cations before and after planting.  Areas receiving applications during
 the growing season had taller crop growth when approaching maturity.

 Feedlot runoff effluent is  of direct benefit in  supplying the water
 requirement of crops.  However,  runoff is not a  dependable  irrigation
 water supply.   Annual precipitation on the Great Plains  tends to be
 below the mean for  3 years  and above for 2 years of five.   This  means
 that disposal  of runoff can be a problem at  times during  the  two wetter
 years  and be in short supply in  the  three drier  years when  water could
 be  used advantageously.  Fortunately,  runoff can be applied in quan-
 tities greater than the crop water requirement without significantly
 affecting crop quality  or yield.

 Special corrosion-resistant pumping  equipment is  not  required for the
 disposal  of effluent.   Centrifugal pumps,  with impellers and  casings  of
 both brass  and cast  iron, have continued  to  function  satisfactorily
 when used with effluent.  Portable,  aluminum pipe has  been used  for
 5 years without  accelerated deterioration.

 The functioning of brass irrigation sprinkler heads has not been im-
paired by runoff effluent.   However, nozzles with small-diameter
orifice, 0,5 cm  (.197 in)   and smaller, have plugged with solids when
the pump suction was on the bottom of the impoundment.


                                   39

-------
 Experience with Holding Ponds

 Separation of solids  from the  runoff prior to storage is desirable.
 Combined  storage of solids  and runoff in a lagoon  leads to odor produc-
 tion  in warm weather.  Pumping the solids and runoff from a lagoon is
 difficult, and drying before removal of the solids is slow and tedious.

 The Omaha site utilized a debris basin, providing  temporary storage for
 runoff and longer-term storage for solids.  Odor production was not
 serious,  but the basin was  essentially isolated from dwellings and work
 areas.  Also, the 15% slope and clay soil of the feedlot surface pro-
 vided an  appreciable  quantity  of suspended soil materials in the runoff.
 The soil  content of the runoff possibly affected degradation and result-
 ing odor  production.

 The holding pond at Gretna has not been a serious  source of odors.
 Limited gas production has been observed with warming weather in late
 spring or early summer.  Surprisingly, odors have been limited in both
 duration  and intensity.  A volume of 16 m3 (20.9 cu yd) of solids was
 removed from the holding pond  on July 23, 1971.  This was the total
 accumulation of solids in the  pond from July 3, 1969, resulting from
 31.3  cm (12.3 in} of  runoff produced by 134.0 cm (52.8 in) of rain
 over  the  2-year period.  An additional 62 m3 (81.1 cu yd) of solids
 from  the  runoff were  collected in the debris basin prior to discharge
 into  the  holding pond.

 The holding pond at Springfield has been an obvious source of odor with
 the first periods of  continued 32.2°C (90°F)  daily temperatures.  The
 settled solids were not removed after construction in 1969 until the
 holding pond was enlarged in 1973.  The relative accumulation of solids
 was much  less than in the holding pond at Gretna.  The debris basins
 at Springfield are even more efficient than the solids trap at Gretna.

 Reasons for differences in odor production at the two sites are only
 speculation.   Wind movement on the hillside at Gretna is unrestricted.
 The Springfield holding pond is on a valley floor,  protected by trees
 and lying immediately adjacent to a building.   Odor dissipation by
 wind movement is definitely restricted at Springfield.  Also,  tree
 leaves fall and crop residues  are blown into the Springfield holding
 pond.  The pond itself is larger in area, receiving about four times
 as much runoff.  The Gretna holding pond has  been emptied periodically
 and the collected solids have dried.   Runoff was stored in the Spring-
 field holding pond to permit maximization of the effluent-utilization
 studies.   Under normal management conditions,  the Sprinfield holding
pond would have been empty and dry during most of the periods when
 odor production was a problem.

 Site selection for a holding pond might include exposure to wind move-
ment.  Sealing of the soil surface after construction of a holding
 pond should not be necessary, even on a permeable soil,  unless a

                                    40

-------
 domestic water well is located in the immediate vicinity.  The organic
 solids in the runoff effluent soon effectively seal the soil surface
 to continued infiltration.

 Holding ponds should not be excesively large, areawise.  As an example,
 storage capacity of 15 cm/ha.(1500 m3) per hectare of feedlot contribu-
 ting area is adequate for most runoff-management systems in eastern
 Nebraska.  The impoundment, however, should be designed for 120 cm or
 more depth of storage rather than a 60- to 90-cm depth.  Reducing the
 area required will reduce weed problems and potential salt problems.

 The first runoff of feedlot flushes much of the readily soluble and
 transportable salts (11,  12).  In a dry season with limited runoff, a
 normal production of salts is available for movement in the lesser
 quantities of runoff.   If storage of such runoff is continued in a
 holding pond with a large surface area subject to evaporation,  the
 effluent eventually applied to the soil may have a high salt  content.

 Experience with Crop Response

 Land  application of the effluent  from feedlot runoff is the most  feas-
 ible  means of disposal  available  CIS,  16).   Land disposal  may decrease
 yield and quality of crops,  increase soil  salinity,  and cause deterio-
 ration of soil  structure.

 A  study of effluent disposal was  initiated  in 1970  at the  Springfield
 site  with crops  of tall fescue and perennial  ryegrass,  both overseeded
 with  Ladino  clover on a silty clay  loam.  The three  species are well
 adapted to eastern Nebraska  and were chosen for  their different toler-
 ances  to  salt.   Tall fescue  has good salt tolerance, perennial ryegrass
 has moderate  salt  tolerance,  and  Ladino  clover has very low'salt  tol-
 erance.   While periodic measurements of  electrical conductivity of the
 surface soils were  made, along with chemical  analyses to measure  salt
 accumulation  in  the soil, it was  believed that the differences in  salt
 tolerance  of  the three species would permit almost immediate detection
 of harmful salt  accumulations in  the soil (17).

 The four  treatments used throughout each growing season were:  (1)  5.1
 cm (2 in} of water  once each week; (2) 2.5 cm  (1 in} of effluent once
 each week; (3) 5.1  cm (2 in} of effluent once each week; and  (4) 7.6
 cm (3 in) of effluent once every  2 weeks.

The amounts of water and effluent applied during the three growing
seasons (1970-1972) are given in Table 8.  Precipitation plus the
applications of effluent and water increased the soil-water content at
the 2.4-m  (2.6-yd) depth on all treatments by the end of July, 1970.
This indicated initial water movement through and below the effective
root zone of the grasses and clover.
                                    41

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Table 8.  FEEDLOT EFFLUENT AND WATER APPLICATIONS TO GRASS AND CLOVER

          PLOTS, SILTY CLAY LOAM SOIL, SPRINGFIELD, NEBRASKA, 1970-72
Year
 Number of
applications
Total depth
  applied
    (cm)
   Total depth
including rainfall4
       (cm)
1970
1971
1972
1970
1971
1972
1970
1971
1972
       5.1 cm water once each week

     10                 50.8
     18                 91.4
     17                 86.4

      2.5 cm effluent, once each week
     10
     18
     17
    25.4
    45.7
    43.2
                  5.1 cm effluent, once each week
     10
     18
     17
    50.8
    91.4
    86.4
                         79.9
                        102.7
                        111.5
       54.5
       57.0
       68.3
       79.9
      102.7
      111.5
                  7.6 cm effluent, once every 2 weeks
1970
1971
1972
5
9
9
38.1
68.6
68.6
67.2
79.9
93.7
 Rainfall during season of application:   29.1 cm (11.5 in}, July 1-
 Sept.  30, 1970; 11.3 cm (4.5 in), June  l-Oct.15, 1971 [40.6 cm
 (16 in)  normal];  and 25.1 cm (9.9 in} June 1-Oct.  1,  1972.
                                 42

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  The  total  quantities of solids,  nutrients,  and salts  applied with the
  various  treatments from July 1,  1970,  to October 1,  1972,  are listed
  in Table 9.   Precipitation totaling 159.8 cm (63 in}  was measured dur-
  ing  this period.   The 5.1-cm-(2-in}  per-week   rate of application
  supplied 31 metric tons (34.1  tons)  of solids  and 3,114 kg (6,866 Ib)
  of nitrogen per hectare over the  3  years.   More  than  1,000 kg (2,205
  Ib)  of N per  hectare per season  appears  to  be  excessive.   However,
  losses of  NH^-N are high immediately after  the application of the efflu-
  ent; only  about one-half of the  total  N  applied  is available  the  first
  year.

  The highest-yielding treatments in  1971  were the  2.5  cm (1  in} of
  effluent weekly and 7.6 cm  (3  in} of effluent  biweekly, with  total
  season yields of 9,440  and  9,440 kg/hectare  (8,420 Ib/acre),  respec-
  tively.  The 5.1-cm (2-in}  water treatment yielded least--  8,438  kg/ha.
  (7,527 Ib/acre).  For all treatments,  average  yields decreased while
 total nitrogen increased with each succeeding harvest.  However,  total
 N did not differ significantly between treatments.

 The plots were harvested May 31,  July  19, September 5, and October 16,
 1972.  Very little ryegrass or fescue remained to compete  with the clo-
 ver in the  spring of 1972.  The last three harvests  consisted entirely
 of Ladino clover.   In 1972, the 7.6-cm (3-in} biweekly effluent treat-
 ment  yielded most,  10,220 kg/ha.(9,116 Ib/acre),  and  the water-irrigated
 treatment yielded  least, 8,460 kg/ha.(7,546  Ib/acre).   Only at the
 second cutting,  however, did the  7.6-cm (3-in}  effluent treatment yield
 significantly more   (5% level) than did the watered treatment.   No other
 differences were significant for  individual  cuttings.   Because of the
 dominance of the Ladino clover, paired subplots planted to  fescue and
 ryegrass  did not differ significantly.   Therefore, the yields  and ni-
 trogen  contents are summarized  for the whole plots in  Table 10.  For the
 seven cuttings in  1971-1972, the  7.6-cm (3-in}  biweekly effluent  treat-
 ment  yielded  19,620 kg/ha.(17,501  Ib/acre, which  was significantly
 higher  than the watered treatment  of 16,900  kg/ha.(15,074 Ib/acre).
 None  of the other differences were  significant.

 A maximum of 229 cm (90 in}  of  beef feedlot  runoff effluent was applied
 during  three growing seasons to the  tall  fescue,  perennial  ryegrass,
 and Ladino  clover.   No detrimental  salt or nutrient accumulations  were
 found in  the silty  clay loam soil at  the  end  of the period.  The
 effluent  applications generally improved  forage yields, despite appli-
 cations in  excess of the water  requirements of  the grasses  and clover.
 Chemical  analyses of the forage did not reveal  undesirable  or  toxic
 contents, and the forage was of excellent quality.  Precipitation  to-
 taled 160 cm (63 in}  during  the period  from July  1, 1970, to October
 1, 1972.

 In the second season, the Ladino clover dominated  the  stands with  the
more salt-tolerant grasses.  This indicated that undiluted  runoff


                                   43

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Table 9.  QUANTITIES OF SOLIDS AND NUTRIENTS APPLIED TO GRASS-CLOVER,
              COCKERILL FEEDLOTS, SPRINGFIELD, NEBRASKA, 1970-72
                                     (kg/ha.)

1970
Total solids
Volatile solids
Total nitrogen
Total phosphorus
Salts
1971
Total solids
Volatile solids
Total nitrogen
Total phosphorus
Salts
1972
Total solids
Volatile solids
Total nitrogen
Total phosphorus
Salts
Total for 3 years,
1970-72
Total solids
Volatile solids
Total nitrogen
Total phosphorus
Salts

2.5 cm weekly

16,820
9,055
902
45
7,482

13,710
5,925
414
196
4,032

9,486
4,312
241
90
3,366


40,020
19,290
1,557
330
14,880
Grass -clover
5.1 cm weekly

3,399
18,120
1,803
90
14,960

27,420
11,860
829
392
8,064

1,898
8,624
482
179
6,726


80,040
38,600
3,114
661
29,750

7.6 cm biweekly

26,410
14,390
1,434
73
11,880

20,560
8,892
622
297
6,048

15,070
6,896
381
146
5,342


55,670
30,130
2,436
515
23,270
                                  44

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Table 10.  FORAGE YIELDS AND TOTAL NITROGEN CONTENTS, GRASS AND CONTENTS, GRASS AND CLOVER EFFLUENT
                       DISPOSAL PLOTS, SPRINGFIELD, NEBRASKA, 1971-1972 a

Treatment
Date of
harvest

June 2,
July 19
Aug. 24
Total -
May 31,
July 19
Sept. 5
Oct. 16
Total -

1971
, 1971
, 1971
1971
1972
, 1972
, 1972
, 1972
1972
Total - 1971-72
2.5 cm effluent
weekly
Yield
kg/ha.
3,377
3,184
2,293
8,854
2,726
2,583
2,205
1,541
9,055
17,910
Total N
\
>
2.10
2.72
3.47

3
2
2
2



.42
.93
.69
.39


5.1 cm effluent
weekly
Yield
kg/ha.
4,112
3,138
2,192
9,442
3,098
2,741
2,100
1,500
9,432
18,870
Total N
%
2.26
2.98
3.62

2.85
2.90
2.90
2.24


5.1 cm water
weekly
Yield
kg/ha.
3,783
2,495
2,159
8,438
2,741
2,376
1,997
1,347
8.460
16,900
Total N

2.
3.
3.

3.
2.
2.
2.


%
89
02
47

08
87
89
42


7.6 cm effluent
biweekly
Yield
kg/ha.
4,061
3,409
1,930
9,400
3,398
3,283
1,939
1,599
10,220
19,620
Total N
%
1.92
2.82
3.64

2.45
2.70
1.93
2.42


     Grasshopper damage in 1970 precluded meaningful forage data

-------
effluent in this area can be used safely to irrigate a crop of  low
salt-tolerance.

Results from this study indicate that the water and nutrients in feed-
lot runoff effluent can be utilized by perennial hay crops.

Corn also was irrigated with both feedlot runoff effluent and water on
the silty clay loam at Springfield.  Five treatments were replicated
three times in a completely random design.  The treatments were weekly
applications of 3.8 cm (1.5 in.) of effluent, 3.8 cm (1-5 in.) of water,
7.6 cm (3 in.) of effluent, and 7.6 cm (3 in.) of water.  About 1 month
after the corn was planted, irrigation furrows were formed between the
corn rows, and the weekly irrigation applications were begun.   Irriga-
tion was discontinued when the corn began to dent in early September
(18).

The total quantities of solids, nutrients, and salts applied to corn
plots receiving maximum rates of effluent application are shown in
Table 11.  The corn grain and stover yields for the various treatments
are reported in Table 12.

The effluent-irrigated treatments yielded more grain and stover than
corresponding water-irrigated treatments and more than the check treat-
ment each of the 3 years.  These differences, however, were not sta-
tistically significant (5% level).  Three years' yield data were
analyzed as split plots in time.  The 3-year average grain yields
showed highly significant differences between the check treatment and
all irrigation treatments.  The effluent treatments averaged 690 to
815 kg/ha. (615 to 727 Ib/acre) more than the corresponding water treat-
ments.  While these differences were not significant at the 5%  level,
the difference between the 3.8-cm (1.5-in) effluent and 3.8-cm water
treatments was significant at the 10% level.  The average for the two
effluent treatments was almost identical, as were the two water treat-
ments.  The 3-year average stover yields were not different among the
four irrigation treatments.  The effluent-irrigated stover yielded more
than the check, but the water-irrigated stover did not.

Chemical analyses of the stalks did not reveal nitrate contents which
could be related to the effluent treatments.

Forage sorghum was irrigated with feedlot runoff effluent and with
water at the Springfield site during 1971 and 1972 (15, 16, 19).

A series of five treatments with three replications of each treatment
were used.  The water and effluent applications were made in irrigation
furrows as with corn.   The treatments are as follows:  (1) check plot,
no application; (2) 2.5 cm (1 inj> water every 5 to 7 days if no rain,
late June to harvest;  (3) 5.1 cm (2 in}  water every 5 to 7 days if no
rain, late June to harvest; (4) 2.5 cm (1 inj) effluent every 5 to 7


                                   46

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 Table  11.   TOTAL QUANTITIES  OF  SOLIDS,  NUTRIENTS AND  SALTS APPLIED TO

            CORN  PLOTS  RECEIVING MAXIMUM RATES OF EFFLUENT APPLICATION
                          SPRINGFIELD, NEBRASKA, 1970-72a
                                      (kg/ha}
; Total
Year ' solids
1970b 21,730
1971C 18,206
1972d 16,740
Total
1970-1972 56,730
; Volatile | Total ; Total
solids ' nitrogen' phosphorus
11,760 1,198 56
7,280 504 336
7,616 414 146
26,666 2,116 538
.' Total
salts
9,677
5,219
5,757
20,653
Quantities of solids, nutrients, and salts for the lower rates of
 effluent applicaton are one-half of the values tabulated for the
 maximum rates of effluent application.

 Values for 11 effluent applications of 5.1 cm (2 in) each.

°Values of 8 effluent applications of 7.6 cm (3 in} each.

 Values for 10 effluent applications of 7.6 cm (3 in.) each.
                                  47

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00
      Table 12. CORN GRAIN AND STOVER YIELDS FROM EFFLUENT DISPOSAL PLOTS, COCKERILL FEEDLOTS, SPRINGFIELD,




                                                  NEBRASKA, 1972

3.8
3.8
7.6
7.6
Irrigation
treatments
cm effluent
cm water
cm effluent
cm water
: Corn grain yields ,
: kg/ha. @15.5% moisture
:
10
9
10
9
1970
,560
,107
,780
,433
•
6
5
6
6
1971
,285
,883
,987
,617
! 1972
11,950
11,420
11,260
10,880
: 3-yr
: average
9,602
8,806
9,671
8,975
: Corn stover yields,
: kg/ha. dry matter
; 1970 ;
8,524
7,665
9,452
7,977
1971
9,470
8,595
8,780
8,502
I 1972
*
11,880
11,460
11,660
11,590
: 3-yr
: average
9,957
9,241
9,964
9,358
      Check
6,567
5,808    10,980
7,784
7,085
8,072
8,695
7,951

-------
 days if no  rain,  late  June  to harvest;  and  (5)  5.1  cm  (2  in} effluent
 every 5 to  7 days  if no rain, late June to  harvest.

 The characteristics of the  effluent and total quantities  of nutrients
 and solids  applied to  the forage with the 5.1-cm  (2-in} effluent
 application are given  in Table 13.  The yields  of the forage are
 presented in Table 14.

 The 2.5-cm  (1 in.) effluent  treatment produced the highest yields in
 each of the 2 years.   The forage yield from the 2.5-cm effluent treat-
 ment was significantly higher than all other treatments in 1972.  The
 addition of 2.5 cm effluent per week (25 cm annually) may be the opti-
 mum effluent application rate for forage production in northeastern
 Nebraska.

 Nitrate-nitrogen contents of plan samples for each respective treatment
 are presented in Table 12.   All  treatments showed high N03-N concen-
 trations in 1971.   These high N03-N concentrations,  however,  could not
 be attributed to effluent loading; dry weather and carry-over of N from
 1970 are possible reasons.

 The N03-N  content  of plant  samples collected from the 1972 harvest shows
 a  great  reduction  in N03-N  in all treatments as  compared with 1971.
 Cool, rainy weather during the  1972  growing season  and lower N soil
 reserve  are  factors partially accountable  for this observation.   Both
 effluent treatments showed  higher NC>3-N concentration than plant samples
 from the water  treatments.   Increased  effluent  loading  resulted in in-
 creasing N03-N  accumulations.  The butt  samples  from plots receiving
 5.1 cm (2  in} of effluent in 1972 were  significantly higher in  N03-N
 than those harvested  from the  5.1-cm  (2-in}  water treatment (Table 15).

 All plant samples  were  anlayzed for Ca,  Mg,  Na,  and  K content.   No
 apparent treatment  differences could be  observed over the  2-year study.
 Potassium concentrations were higher in  all  treatment samples collected
 in  1971, ranging from 2.13%  (2.5  cm effluent) to 2.30%  (5.1 cm water),
 as  compared  with the range of  1.75% to 1.93% in  1972.  The  differences
 were not related to treatment.

 The  sodium-bicarbonate-extractable P content of  the  top  10.2 cm  (4 in}
 of  soil cores taken in  1971  and 1972 was determined.  An additive effect
 was  observed from the application  of feedlot effluent.  The P increase
 was  observed only in the surface soil samples.   Analyses of soil  cores,
 taken to a depth of 2.4 m (2.6 yd) revealed  little variation of  P  lev-
 els below the 10.2-cm (4-in} soil depth between  treatments.

The P addition from the applied effluent was significantly higher in
the 5.1-cm (2-in} effluent treatment when compared with both water
treatments  in 1972.
                                    49

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Table 13.  CHARACTERISTICS OF THE EFFLUENT AND TOTAL QUANTITIES OF NUTRIENTS AND SOLIDS APPLIED

                   TO FORAGE SORGHUM PLOTS IN 1971 AND 1972, SPRINGFIELD, NEBRASKA

1971
Average
kg/ha, from 5.1-cm
applications
(56 cm)
1972
Average
kg/ha, from 5. 1-cm
Volatile :
solids : Ash
% : %
0.11 0.12
5924 6764
0.09 0.11
4424 5432
Total
N
ppm
71
399
48
242
rNH^-N,
: ppm
66
366
21
106.4
N03-N,
ppm
1.13
12.3
4.7-2
23.5
N02-N,
ppm
0.08
0.45
0.04
1.20
Total : Electrical
P „ : conductivity,
ppm P : mmhos/cm
34 8.9 1.51
192.6
18 9.0 1.26
90.7
  application
  (51 cm)

-------
          Table 14.  FORAGE SORGHUM YIELDS FOR 1971 and 1972

                         (metric tons dry matter/hectare)
Treatment
Check
2.5 cm water
5 . 1 cm water
2.5 cm effluent
5. 1 cm effluent
1971
15.2
16.1
17.2
17.5
17.0
1972
15.5
15.5
14.8
18.1
15.5
              Duncan  Multiple  Range  Test  of sorghum  yields
                     at  the  5% level of significance*
           1971
Treatment
Yield
                               1972
Treatment
Yield
2.5 cm effluent      17.5 a

5.1 cm water         17.2 a

5.1 cm effluent      17.0 a

2.5 cm water         16.1 a

Check                15.2 a
                     2.5 cm effluent     18.1 a

                     5.1 cm effluent     15.5 b

                     2.5 cm water        15.5 b

                     Check               15.5 b

                     5.1 cm water        14.8 b
*Note:  Yields followed by a different letter (a or b)  were signifi-
 cantly different at the 5% level.
                                   51

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TABLE 15.   NITRATE-N CONTAINED IN FORAGE SORGHUM HARVESTED IN

                       1971 AND 1972

Treatment

Check
2.5 cm water
5.1 cm water
2.5 cm effluent
5.1 cm effluent

1971
Butt
11,700
11,300
10,400
10,800
10,500
N03

Top
3,100
4,380
4,220
3,900
4,200
-N a

Butt
6,000
5,400
4,700
6,100
7,050

1972
Top
2,090
1,680
1,510
1,840
2,020
o
  NO--N calculated on 100% dry-weight basis
    •J
              Duncan Multiple Range Test of NO -N in butt
              samples harvested in 1972, at the 5% level
              of significance
          Treatment                                NO^-N (ppm)

          5.1 cm effluent                             7,050

          2.5 cm effluent                             6,100

          Check                                       6,000

          2.5 cm water                                5,400

          5.1 cm water                                4,700
                                 52

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 The N03-N levels in 2.4 m (2.6 yd) soil cores showed an overall decline
 during the 2-year study.  A sharper decline in NO^N was observed in 1972
 when compared with 1971.  The higher amounts of natural precipitation
 in combination with continued irrigation,  may have facilitated leaching
 of N03-N in 1972.  The fact that the effluent treatments showed less
 decline in NOs-N when compared with the water treatments indicates  that
 some of the effluent- added N was accumulating as
 Additional N losses via plant uptake,  volatilization,  and denitrifica-
 tion may have counterbalanced the N addition in the  effluent  treatments.
 Higher precipitation occurring in 1972 again may have  been the  influ-
 encing factor when these losses are considered.

 Soil pH and electrical conductivity analyses were conducted on  soil
 samples to a depth of 20 cm (7.9 in).   Slight increases  in both soil pH
 and electrical conductivity were observed  on effluent-treated soil.  The
 increases were slight, however, and would  cause no detrimental  effects
 on  crop production.

 Analyses of soil  solution samples showed an  increase in  concentration of
 Ca,  Na,  and K ions in effluent-treated soil.   These  cations were increas-
 ing in soil solution samples collected at  a  depth of 61  cm (24  in).
 Samples  collected at a depth of 1.8 m  (2 yd)  did not follow this pattern
 and showed little difference among treatments.

 The  increase  in Ca,  Na,  and K observed in  soil  solution  samples from
 effluent treatments  may account for the increase in soil pH and elec-
 trical  conductivities.   The increases  in pH  and  electrical conductivities
 were  slight but did  reflect some  salt  addition due to effluent  applica-
 tion.

 The physical properties  of the  soil  on which  the  forage  sorghum was pro-
 duced with  the applications  of  runoff  effluent were also investigated.
 Soil samples from 0-  to  10-cm (3.9-in)  depths were taken for bulk den-
 sity, particle size  analysis, moisture  release,  hydraulic  conductivity
 of disturbed and  undisturbed  samples,  and wet-aggregate  analysis.  These
 soil samples were  taken  just  before, midway,  and  at the  end of each
 irrigation  season.  The  effluent  treatments produced no  differences in
 bulk density, soil water storage  and release, or  in wet-aggregate analy-
 ses.  Significant  differences were measured for hydraulic  conductivity
 of disturbed and undisturbed  soil samples.

 The hydraulic conductivity values on disturbed soil surface samples
were recorded at the  2-  and 24-hour intervals.  The ratios of the 3 hr:
 24 hr values were  calculated.  A  small ratio indicates low stability of
 aggregates  in water and, hence, the physical condition of soil has  de-
 teriorated.  Significant differences were discovered at the 1% level
for treatments of nonirrigation vs others and water vs effluent.  A de-
crease in hydraulic conductivity was noted  for the effluent plots as

                                   53

-------
compared with the nonirrigated plots.  This is probably associated with
the clogging of pores by the colloidal particles and the dispersion of
soil by the sodium and potassium in the effluent.  A decrease could also
occur from organic matter in the effluent.

An important fact was also noted in comparing the hydraulic conduc-
tivities for the fall 1971 with spring 1972 samples.  The fall samples
show a definite decrease in hydraulic conductivity ratios of effluent
plots compared with nonirrigated plots, while in the spring, the ratio
values are nearly the same for all treatments.  Evidently, over the win-
ter period the effects of effluent are reduced to nearly normal,
probably through leaching of the salts by winter rains.  The freezing
and thawing of the soil also increases the water stability of
aggregates.

Percolate samples, representing the first 50 ml, were collected while
the hydraulic conductivities were analyzed.  A chemical analysis was
conducted for Na , K , Cl", N03-N, NH^-N, pH, and electrical conduct-
ivity.  The highest value sodium content was 116 ppm for the 5.1-cm
(2-in.) effluent plots after the final irrigation in 1971.  This value
does not create any immediate problems in deterioration of the physical
properties of the soil.  All sodium values in the spring of 1972 were
lower than the previous fall.  These were reduced by leaching over the
nonirrigation season.

The high-effluent plots recorded the largest potassium content, with
123 ppm after the first irrigation season being the highest.  Leaching
during the nonirrigation season reduced the potassium values by at
least half.

Chloride contents were calculated and show rather large values for
effluent plots in 1971, but very reduced values in 1972.  Precipitation
during the nonirrigation season caused the leaching of Cl~, as the
chloride ions are very susceptible to leaching.
The results for NH^-N, NOs-N, and pH show no serious changes from
application of effluent,, as the values are all low or normal.

The highest electrical conductivities (EC) for the percolate samples
were obtained on the effluent plots.  These values were at least double
the values of the water and no-irrigation (check) plots, but still low
enough not to be a salt problem.  The EC of the percolate from the
effluent plots decreased during the nonirrigation season of 1971-72.
The decreased EC shows that some salts were probably leached during
this period.

Feedlot runoff effluent is a highly variable, low-grade fertilizer.
However, large and frequent applications can supply much of the
                                  54

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nutrient needs of many crops.  Annual applications up to 91.4 cm
(36 in.) on grass-Ladino clover and 76.2 cm  (30 in} on corn have not
decreased, and sometimes increased, yields.  Good growth of the Ladino
clover, a low salt-tolerant crop, indicates salt accumulation in the
soil is not a problem.
COLORADO CONDITIONS

The limited runoff is of such composition that it must be kept out of
surface waters, and disposal on arable land is preferred.  No data are
available concerning direct application to crops, but judging from com-
parisons made of the compositions of Nebraska and Colorado runoff, the
Colorado material would have to be diluted with irrigation water to
lower the conductivity to acceptable values if such disposal were
contemplated.
                                 55

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                              SECTION VIII

  COMPOSITION OF SOIL SOLUTION AND SOIL ATMOSPHERE BENEATH FEEDLOTS

NEBRASKA

Solution and Gas Samples from Caissons

Prior to these studies, it was believed most feedlots contaminated soil
profiles and water tables beneath them.  The data presented here were
obtained from soil solution and soil gas samples collected from caissons,
vacuum lysimeters, and soil cores.  Soil solution samples were used to
assess pollutants that may be moving through the soil profile and soil
gas samples were used to determine the reduction status of the soil
profile.

At the Central City site, there were two caissons in the feedlot and one
in an adjacent cropped field.  At the Springfield site, there was one
caisson in the slope, one in the basin of the feedlot, and one in an ad-
jacent cropped field.  Caissons design and use have been described (5).

Data from the Central City feedlot (Table 16) show a comparison of
average yearly concentrations of the N compounds beneath a feedlot and


 Table 16.   AVERAGE YEARLY CONCENTRATIONS OF SOME NITROGEN COMPOUNDS IN

            THE SOIL SOLUTION BENEATH A FEEDLOT AND A CROPPED FIELD
                                 Cyg/ml)
       Depth,  cm
N03-N
NH4-N
Total N
 Feedlot
 Field
        15.0
        45.7
        76.0
       106.6
        30.5
        61.0
        91.4
32.5
 0.1
 0.3
 0.6
 8.1
 7.2
 7.8
538.6
 30.9
  1.9
  1.0
  8.3
  0.9
  1.1
713.4
 40.6
  8.9
  5.6
 17.1
 20.4
 12.9
                                   56

-------
  a cropped field.  The feedlot N03-N values at 45.7 cm (18 in) and below
  appeared lower than those obtained from the cropped field.  The NHi+-N
  samples from the feedlot and field were similar at 76 cm (30 in) and
  below.   At these depths, total-N values seem to be higher in the field
  than in the feedlot.   However,  the total-N values include the NOa-N
  values, which were higher in the cropped field.   If the  N03-N values
  are subtracted,  the total-N values from 76 cm (30 in)  and below in the
  feedlot and the  cropped field would be comparable.

  The soil water samples indicate this feedlot contributes low amounts of
  NOs-N,  NHjj-N,  and soluble N-containing compounds to the  groundwater.
  Samples from the feedlot obtained at the 15-cm depth were higher in
  these compounds;  however,  at the 76-cm depth,  the levels appeared as
  low as,  or  lower than,  comparable field samples  (20).

  Table 17 shows the  average gas  composition of  the soil atmosphere at
  various  depths beneath the Central  City feedlot  and in an adjacent
  cornfield for  a  1-year period.   High  CHi,  and C02  were found  beneath  the
  feedlot.  As sample depth  increased,  CHit  values  increased to about 18%
  from the 91.4-cm  (36-in.) depth  to 137-cm  (54-in^  depth.   These results
  indicate vigorous CHi+ production  was  taking place in the  feedlot  soil
 profile.  Because CH^  is lighter  than air, only  limited  downward  diffu-
 sion would be expected;  thus, some CH^ was probably produced near the
 137-cm  (36-in.) level.  Single values at the 152.4-cm (60-iru) depth of
 up to 55% CHi+ and 40% C02 were recorded.  Lower concentrations of CH^
 at the surface hint of CHi+ diffusion through the surface  and/or inhibi-
 tion of CH^-producing bacteria by Oa-  Production of the quantities of
 CH^ detected beneath this feedlot indicates the presence of appreciable
 metabolizable organic matter in the soil profile.  This conclusion is
 made on  the basis that CHi» bacteria generally require specific organic
 substrates (21).   As would be expected, 02 concentrations are much
 reduced  because CHi+ production takes place only under anaerobic con-
 ditions.  Where CH^ was high in  individual samples, 02  was very low or
 zero.  Table 17 also shows the cropped field values. No  CH^ was detec-
 ted at any time,  and Q£ and N2 values were close  to atmospheric.   As
 expected, C02 values in the field soil profile were higher than atmos-
 pheric values (22).

 The soil solution data from the  Central City site show  the feedlot is
 not contaminating the  shallow groundwater; therefore, the answer is one
 of  management.  This feedlot is  used continuously through the year.
 The surface  of  the feedlot, when the manure pack  is  intact,  has  a low
 infiltration rate  (4).   Thus,  it seems  that if  a  feedlot  is  kept  well
 stocked  and  manure-packed,  soil  interface  is not  disturbed,  only
 limited  organic matter and  NOa-N will  reach the underground  water
 supply (20).  Also, the feedlot  soil profile should  remain anaerobic.
 The gas  data  from  this  site show the  feedlot profile is reduced,  and
 this indicates denitrification can occur  (22).  Investigations at  this
 site show that groundwater  pollution  from  an active  feedlot  surface is
not a problem.

                                   5-7

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    Table 17. AVERAGE SOIL ATMOSPHERE COMPOSITION AT VARIOUS SOIL DEPTHS

           BENEATH A FEEDLOT AND CROPPED FIELD FOR A 1-YEAR PERIOD
                                (% by volume)
Depth, cm
Feedlot
30.5
45.7
61.0
76.0
91.4
106.6
122.0
137.0
Cropped field
30.5
61.0
91.4
122.0
152.4
C02

15.0
12.5
15.0
23.0
18.5
18.0
18.5
21.0

2.0
2.0
2.5
2.5
1.0
02

9.5
9.5
7.5
4.5
5.0
5.0
5.0
6.0

18.0
18.0
18.0
18.0
19.0
N2

66.0
68.5
65.0
45.0
58.5
57.5
56.5
52.0

79.0
80.0
79.0
79.0
79.0
CH4

8.0
8.0
11.5
27.5
18.0
17.5
18.5
20.0

0
0
0
0
0
Total

98.5
98.5
99.0
100.0
100.0
98.0
98.5
99.0

99.0
100.0
99.5
99.5
99.0
(These data show this  feedlot soil profile is favorable for denitrification)
                                    58

-------
 Figure 11 shows NOs-N increased in the basin at the Springfield site
 through the 122-cm (48-in^J depth during the first 3 months of sampling
 (11 months of operation].  Values up to 70 ppm NOs-N were recorded at
 30.5 cm (12 in} while samples at 61 and 122 cm (24 and 58 in.) peaked
 at about 40 ppm NOa-N.  After 4 months, NOa-N increased to approximate-
 ly 40 ppm at 152.4 cm (60 in.) and was decreasing at 122 cm (48 in} .
 After 13 months of sampling (21 months of operation), soil water
 nitrate had decreased to 1.4, 10, and 12.5 ppm NOa-N at 61, 122, and
 152.4 cm (24, 48 and 60 in.), respectively.  Near the end of the study,
 the soil water samplers ceased to function at 30.5 cm (12 in.).  Soil
 water nitrate at 183, 244, and 305 cm (72, 96, and 120 in) was rela-
 tively constant at respective averages of <1, 15,  and lOppm N03-N
 (Figure 12).   Two unexplained high values caused the rise at 244 cm
 (96 in.) in March.  These data show nitrate was not carried below 152.4
 cm (60 in}  (23).

 The decrease  in nitrate during the latter part of the sampling period
 coincided with an increase in C02 and a decrease in 02  (Figure 13).
 The C02 was highest between 61 and 305 cm (24 and  120 in^.  These  data
 indicate establishment of reducing conditions beneath the basin.   Re-
 ducing conditions, coupled with the nitrate decrease,  indicate that
 denitrification was occurring.  Nitrate-N of the well samples was  below
 the U.  S.  Public Health Service limit of 10 ppm (24).

 These  studies  indicate if a feedlot is stocked continuously,  and when
 cleaned,  if the dense soil-manure interface layer  is  not  removed,
 pollution of groundwater should not occur.
COLORADO

Solutions and Gas Samples  from Caissons

Cased, dry wells or caissons were installed in  a commercial feedlot
(Ashlind Feeders, Inc.,  9.3 km (5.8) miles northeast of Fort Collins)
late in 1970.  One caisson was installed near the feedbunk  (low eleva-
tion in a pen), one caisson was installed near  the center of the same
pen (at a higher elevation), and one in an adjacent alfalfa field for
comparison observations.   Soil water tensions,  soil temperatures, soil
gases were monitored.  In  addition, water in the general area from
irrigation wells, irrigation canals, drainage canals, and domestic
wells was analyzed for comparison with the caisson data.

Data are still being gathered and analyzed, and Tables 18 through 25
present the current results.

Tables 18-20 present the composition of extracted soil solutions
obtained by porous ceramic cups and the water samples for comparison.
                                  59

-------
                                          DEPTH   OF  SAMPLE  FROM  SOIL
                                                  o  30 5        SURFACE,  cm
                                                  ,  61.0
                                                  A I 22
                                                  A 152.4
                                 N
D    J     F    M
 TIME,  months
M
Figure 11.  Average N03-N  levels in the soil solution extracted from the broad-basin terraced
              feedlot at  increments of depth and time, Springfield,  Nebraska,  1970-1971.

-------
            £
            ex
    60


    70


    60


    50


    40


    30



    2O


    10
                                 DEPTH   OF  SAMPLE  FROM SOIL

                                         0  l83       SURFACE,  cm
                                         o 244

                                         A 305
                                  N    D   J    F    M    A

                                         TIME, months
                                                    M
Figure 12.
Average N03-N levels in the soil solution extracted from the broad-basin terraced

   reecuot at increments of depth and time, Springfield, Nebraska, 1970-1971.

-------
            100

             90

             80

             70

             60

             50
              30
              20
              10
o   C
                                N    D    J   F   M
                                   TIME,  months
Figure  13.  Average soil-gas  composition from 1 to 10  ft. beneath the basin, broad-
                     basin terraced feedlot, Springfield, Nebraska, 1970-1971.

-------
to
    Table 18.  NITRATE AND NITRITE NITROGEN AND ECLECTRICAL CONDUCTIVITY OF SOIL SOLUTIONSa
               OBTAINED FROM CAISSONS AT ASHLIND FEEDERS, INC., FORT COLLINS, COLORADO
Depth,
cm
15
61
91
183
274
wt.b
NOa-N, ppm
Alfal£ab
28
12
3
3
3
2
Bunk
1
2
2
0
3
7
Center
1700
200
78
11
16
11
N02-N, ppm
Alfalfa
0.035
0.040
0.026
0.030
0.025
0.023
Bunk
0.230
0.096
2.600
0.012
0.200
0.060
Center
2.000
0.093
0.180
0.140
0.130
0.066
EC, mmhos/cm @
Alfalfa
3.4
4.6
6.4
6.9
9.9
6.9
Bunk
6.5
2.6
4.6
4.3
4.4
4.0
25 °C
Center
23.6
6.6
5.6
3.8
4.4
4.0
             values  for samples obtained in 1971,  1972,  and 1973
        Soil  solutions obtained from water table or as  low as  possible  in  the  caisson

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Table 19.  CHEMICAL OXYGEN DEMAND, PHOSPHATE, AND pH of SOIL SOLUTIONS  OBTAINED FROM
                  CAISSONS AT ASHLIND FEEDERS, INC., FORT COLLINS, COLORADO
Depth,
cm
15
61
91
183
274
Wt.b
COD, mg02/l F
Alfalfa
79
72

86
180
130
Bunk

290
320
84
92
50
Center

160
120
140
88
37
Alfalfa
0.29
0.45
0.64
0.19
0.17
0.18
'Oj^3, ppm
Bunk

0.51
0.66
0.21
0.12
0.13
Center

0.17
0.12
0.14
0.14
0.15
Alfalfa
8.2
8.2
8.5
8.4
8.6
8.6
PH
Bunk
7.9
7.9
8.0
8.2
8.1
8.1

Center
8.1
8.1
8.2
8.0
8.1
8.1
 Mean values for samples obtained in 1971, 1972, and 1973.
 Soil solutions obtained from water table or as low as possible in the caisson.

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Table 20.  NITRATE AND NITRITE NITROGEN, ELECTRICAL CONDUCTIVITY,  CHEMICAL OXYGEN DEMAND,
            PHOSPHATE, AND pH OF WATER SAMPLES OBTAINED FROM SEVERAL SOURCES IN THE AREA
                 OF THE CAISSONS AT ASHLIND FEEDERS, INC., FORT COLLINS,  COLORADO
Site Description
Drainage from alfalfa
Drainage from cultivated field
Canal connecting reservoirs
Drainage from pasture
Irrigation well
Cattle pen water tank
NH3-N
ppm
2.5
4.6
3.4
0.2
1.6
0
N02-N
ppm
0.032
0.052
0.031
0.0
0.0
0.0
EC
mmhos/cm
2.4
3.7
2.5
1.0
2.3
0.4
COD
mg02/l
30
40
60
50
40
1100
PO^3
ppm
0.06
0.08
0.20
0.08
0.06
0.62
pH
7.9
7.8
8.1
8.0
8.1
7.1

-------
ON
O\
        Table 21.   CHARACTERISTICS OF SOIL TAKEN FROM NEAR THE CENTER CAISSON AT ASHLIND FEEDERS, INC.

                                               FORT COLLINS, COLORADO
Depth :
cm :
0
76
15.
22
30
38
46
53
-7.6
-15.2
2-22
- 30
- 38
- 46
- 53
- 61
Water
Content ,
% DWBa
10.
11.
12.
12.
14.
16.
16.
15.
0
6
6
6
0
1
1
6
: Soil Solution :
; N03-N + N02-N I
ppm
0.
79.
109.
80.
67.
54.
34.
32.
0
4
0
9
4
1
2
2
Oven- dry Soil
N03-N + N02-N
ppm
0.
9.
13.
10.
9.
8.
5.
5.
0
2
7
2
4
7
5
0
ppm
568.
221.
34.
5.
2.
3.
1.
4.
Basis


N pH
6
2
6
3
7
2
8
6
8.
7.
7.
7.
7.
7,
7.
7.
43
75
74
78
82
88
89
90
       a
         Dry weight basis

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Table 22.  SOIL WATER TENSIONS (CENTIBARS) AS QUARTERLY AVERAGES FOUND IN THE ALFALFA
                    CAISSON AT ASHLIND FEEDERS, INC.  FORT COLLINS, COLORADO
Depth
cm
IS
61
91
183
274
*
*
: 3
40.2
45.5
59.5
24.5
24.7
1971

4
19.6
39.2
66.8
25.0
26.5
•
*

: 1
25.0
14.6
46.1
27.0
31.4
1972

2
32.2
36.3
44.5
27.0
35.7

3
43.8
17.2
29.6
48.8
55.9

4
9.8
0.0
0.0
23.0
57.6


: 1
12.
18.
4.
17.
31.
1973


2
8
7
0
0

2
19.1
27.2
26.5
15.7
27.6

3
22.1
46.1
a
17.2
23.1

4
15.2
31.1
30.8
22.2
23.5
  Tension exceeded 70 centibars and water films establishing tension were  lost.
Table  23.  SOIL WATER TENSIONS  (CENTIBARS) AS QUARTERLY AVERAGES FOUND  IN THE  BUNK  CAISSON
                           AT ASHLIND  FEEDERS, INC.,  FORT  COLLINS,  COLORADO

cm
15
16
91
183
274

3
51.0
39.6
35.2
13.9
0.0
1971
4
57,0
51.4
31.7
17.7
5.4

...
: 1
53.6
54.0
33.9
19.5
8.9

2
51.6
50.8
33.7
19.3
8.5
1972
3
46.7
44,0
30.9
14.9
2.3

4
53.9
48.0
31.6
18.9
7.6

1
48.6
48.3
22.5
20.3
9.5
19
2
46,1
44.9
23.0
20.1
8.3
73
3
38.4
35.0
20.8
13.4
2.8

4
46.4
41.5
20.4
18.8
6.7

-------
00
      Table  24.   SOIL  WATER TENSIONS (CENTIBARS)  AS QUARTERLY AVERAGES FOUND IN THE CENTER CAISSON
                                AT ASHLAND FEEDERS, INC.,  FORT COLLINS, COLORADO
Depth
cm
15
61
91
183
274
Table 25.

Location
Alfalfa
Bunk
Center
I 1971 1972 1973
:34 123 4 1234
33.8 19.0 23.0 24.0 29.6 41.5 38.2 37.6 36.1 47.8
23.8 16.3 20.0 22.0 25.2 29.4 29.2 28.7 27.5 36.2
21.5 14.5 18.1 19.8 21.8 24.3 24.2 24.2 22.8 29.0
15.8 16.4 20.8 22.0 19.3 21.2 24.2 24.2 18.2 21.7
10.7 14.4 16.9 17.3 12.4 15.9 17.6 17.5 11.4 16.1
AVERAGE SOIL ATMOSPHERE COMPOSITION (PERCENT BY VOLUME) BENEATH A CROPPED FIELD
AND FEEDLOT FOR TWO YEARSa AT ASHLIND FEEDERS, INC., FORT COLLINS, COLORADO
°2 N2 c°2 CHi* Total
18.6 80.7 0.6 0.0 99.9
3.7 74.1 16.7 5.4 99.9
5.8 82.4 11.7 0.0 99.9
        Means of 72 determinations over 4 depths.

-------
 The COD, POi^3, and pH data from the feedlot caisson showed no signifi-
 cant differences when compared with the control caisson in the alfalfa
 field.  There were no marked differences in COD and POi^3 between the
 feedlot and control caissons.

 The data that showed important, but not alarming, differences are in
 Table 18 for soil solutions.   For the center caisson, the concentra-
 tions of N03-N were very high near the soil-manure interface, but these
 sharply decreased with depth.  The groundwater beneath the lot had NOs-N
 contents ranging from 7 to 11 ppm.  Stewart et al. (25)  found the aver-
 age NOs-N content to be 10 ppm in groundwater in northeastern Colorado.
 Headden (26)  reported that samples of groundwater from the Fort Collins
 Agricultural  Experiment Station ranged in NOs-N concentration from 1
 to 14 ppm.

 One can explain the decline of NOs-N with depth at the center caisson
 by considering the data in Tables 20-24 in conjunction with knowledge
 of the nitrifying bacteria in the soil.   Note that in Tables 22,  23,
 and 24 the  upper soil profile water tensions in the feedlot were  fairly
 constant over the year.   There were no pulses of water percolating in
 the feedlot as compared to the cropped alfalfa.   The upper soil pro-
 file was quite dry (it was difficult to obtain soil solution samples
 with the ceramic cups).   With a low soil water content,  NOs-N movement
 is  principally by diffusion,  a slow process  in soil.   Data in Table 21
 showed that the peak in NOs-N concentration  was  reached  at a soil  depth
 of 15.2 to  20.3 cm (6 to 8 in).   In fact,  the nitrifying bacteria  were
 inhibited near the soil-manure interface because of a combination  of
 factors:  low  oxygen tension (see  Table 25);  high osmotic tension of the
 soil  solution (see EC in Table 18 and  low water  content  in Table 21);
 and toxicity  of NHs due  to the high pH.   Consequently, both the forma-
 tion and the  movement of NOa-N were severely limited.  As  the  NOs-N
 diffused away from the locus  of formation, the  low-oxygen  tension
 environment favored denitrification,  and little,  if any, N03-N reached
 the water table.   At the bunk site,  nitrification was  seemingly even
 more  restricted,  and the groundwater had more NOs-N than the  soil
 solutions from high in the profile.

 The  intact  manure  pack was  surprisingly  stable and longlived  as a  sys-
 tem  to  seal the soil  so  long  as there  was  sufficient moisture  and
 animal  traffic.  An intact  column  of manure pack  and underlying soil
 has been observed  for  over  14 months in  the  laboratory.  The  only  treat-
ment has been  the  addition  of 6.35  cm  (2.5 in) of water  over  the obser-
vation period  and  firming  the  surface  (to  simulate  animal  traffic).
The manure pack continued  to  generate  CHi*  and maintained a very low 02
 content of  about 1  to  2% in the soil below.

Composition and Amount of Percolate Using Vacuum  Lysimeters

As anticipated at  the beginning of the experiment,  the Anderson (flat)
site allowed the most  significant percolation.  Percolation rates

                                  69

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 ranged  from  0.03  to  3.0  cm  C-01  to  1.2 in.) per year over the study
 period.   It  should be noted that precipitation accounted for only 54%
 of the  total water applied  to  the feedlot during the study period.  The
 remainder, or  nearly half,  of  the applied water was through animal
 excretion.   The average  annual stocking rate  at this site was about
 32.5  square  meters (350  ft2) per animal.  With a higher stocking rate,
 the fraction of water applied  as precipitation would be even less,
 because  a large fraction of the  water would be applied by animal excre-
 tion, and soil water patterns  correspond well with animal traffic
 patterns.  Areas  near the feedbunk  are continually moist.  However,
 this  surface moisture pattern  does  not indicate the pattern of deep
 percolation.   Areas  near the dry center of the lot had approximately
 10 times  the percolation of  the  wet area adjacent to the bunk, in-
 dicating  that  the maintenance  of a  wet manure pack effectively sealed
 the soil  surface.  During the  study, the location of the feeding area
 was moved, resulting in  drying of the manure pack over the lysimeter
 initially in the  "bunk area."  As a result of this drying, the perco-
 lation rate  increased over  a period of several months to a level
 comparable to  that in the center of the lot.  This observation suppor-
 ted a previous hypothesis that alternate wetting and drying resulting
 from partial-year operation contributes considerably to the potential
 pollution from a  cattle  feedlot.

 During the study  period, the total, weighted percolation averaged
 0.5% of the  total water  applied  to  the surface, or about 0.25 cm (0.1
 in.) per year.

 At  the Ashlind site, no measurable percolate was collected at the 75-
 cm  (30-in.) depth  of  installation of the lysimeters.  This conclusion
 is  supported by results of neutron  soil water analyses, of which Fig-
ure 14 is typical.  Although the water content in the upper 75 cm of
 soil was  increased significantly by the rainfall events, this water
was subsequently  lost to evaporation with no significant changes appar-
ent in soil water content at deeper depths.   During this same sequence
of  events, soil water measurements near the feedbunk showed virtually
no  change with time,  further substantiating that the moist manure pack
forms an effective seal.   The chemical composition of leachates ob-
tained from the lysimeters at the two locations is presented in Tables
 26  and 27.

Values for all determinations were comparable to those to be shown
later for the caissons for soil solutions.   The lysimeters at the
sloping Ashlind site  never yielded sufficient leachate for determina-
tion of all the analyses, and by the end of 1971,  the level,  Anderson
lysimeters also had no leachates.
                                  70

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                 VOLUME WATER CONTENT - %
                         10
             100
          E
          o
          I
             200
             300
                    8/18
20
30
                              9/30^
                                         9/23
    8/18-  9/23/69
    4.47 cm
    PRECIPITATION
Figure 14.  Water content profile near center of lot at sloping site.

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Table  26.  CHEMICAL COMPOSITION OF LEACHATES OBTAINED FROM VACUUM
             LYSIMETERS  IN FEEDLOTS NEAR FORT COLLINS, COLORADO
Lysimeter Location
Measurement
EC (mmhos/cm)
at 25°C
PH
N03-N (ppm)
N02-N (ppm)
MVN (ppm)
N (total ppm)
3
P03
P (total ppm)
COD (mg02/l)

Bunk
2.75
7.68
1.83
0.250
0.93
12.28
0.245
0.755
358.2
Anderson
Intermediate
2.45
7.71
4.11
0.232
0.11
10.33
0.220
0.970
750.0

Center
11.29
6.26
767.33
0.081
5.38
887.36
0.170
1.033
3230.0
Ashlind
(Composite)
2.03
7.63
4.46
0.025



565.0
Table 27.  CHANGES OF COMPOSITION OF LYSIMETER LEACHATES WITH TIME
                         FROM CENTER OF ANDERSON FEEDLOT
Date
6-25-69
8-6-69
9-3-69
11-6-69
4-14-71
10-8-71

Volume
(ml)
260
570
47
340
50
13

EC, mmhos/cm
at 25°C
6.72
18.20
19.40
23.00
0.20
0.22

PH
7.30
7.20
4.40
4.10
7.00
7.60

NH3N
(ppm)
280.0
1,550.0
1,630.0
1,144.0
0.0
0.0
                                   72

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 The leachates from the center lysimeter at the level site showed a
 fluctuation in EC, pH, and NOa-N over the period of operation.   These
 changes are characteristic of a pulse of water and favorable nitrifica-
 tion conditions followed by restricted water movement and unfavorable
 nitrification (Table 27).

 The small area enclosed by each vacuum lysimeter produced only  small
 amounts of liquid, thus limiting the frequency of sampling as well as
 the number of determinations per sample.   In general, the limited data
 showed little, if any, contaminants moving through the soil profile
 with an intact manure pack.

 The lysimeter located in the center of the level feedlot  showed a
 fluctuation in flow and composition of leachates suggestive of  an
 initial failure to have a tight manure pack over the lysimeter.   During
 the time of a poor pack there was considerable flow of water with high
 nitrate concentration.  As soon as the manure pack was established,
 both flow and nitrate concentrations were  markedly reduced.

 Experimental Feedlot and Lysimeters at Colorado State University
   Animal Science Facility

 An experimental  feedlot equipped with butyl,  rubber-lined,  soil pits,
 or lysimeters, was completed early in 1973.   Data collection has  just
 started for the  composition of soil solutions  and gases,  and only
 tentative ideas  can be drawn from the data (Tables  28  and 29).

 The  soil pits  were filled with four combinations  of soil  as  shown in
 Table  28,  with two replications  of each treatment across  the center
 of the lot and at  the bunk,  for  a total of 16  pits.  The  pits were
 fitted with ceramic vacuum extractors and  gravity drainage  to obtain
 soil solutions and gas diffusion tubes  to  sample  soil  gases.  The
 analytical data  for soil  solutions  draining by gravity are presented
 in Table 28.   All  the solutions  obtained were  low in NOa-N  and low in
 conductivity.  There  was  no  evidence  of appreciable  movement of NOa-N
 in the  artificial  profiles.

 In Table  29, the soil  gas  data show the effects on gas diffusion  and
 component  concentrations  by  the  two different  fill materials and  their
 relative placement  to the  manure pack.  For example, compare the
quantity of CH4  at  91  cm  (36 in)  in treatments  1  and 2.   CH^ was high
 in the  sand and very  low  in  clay  loam.  Comparison of  the results at
 91 cm  (36  in}  in treatments  3  and 4 indicates  the restriction of CH^
diffusion  by clay  loam  and its relative ease in sand.  Also, these
data indirectly suggest the  locus of  CH4 formation was principally in
the manure pack.
                                   73

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Table 28.  NITRATE AND NITRITE NITROGEN, ELECTRICAL CONDUCTIVITY
           AND pH OF SOIL SOLUTIONS OBTAINED FROM LYSIMETERS OF
           EXPERIMENTAL FEEDLOT AT FORT COLLINS, COLORADO, RIGDEN
                    FARM,  COLORADO STATE UNIVERSITY
Measurement
Treatment
description
1
Clay loam
2
Sand
3
Clay loam
over sand
4
Sand over
clay loam
Bunk
Center
N03-N, ppm
0.49
0.96
2.11
0.30
0.41
1.25
N02-N, ppb
12.8
62.7
228.7
12.3
40.3
90.5
EC
mmhos/cm
0.95
1.10
0.82
0.81
0.98
0.89
pH
8.01
7.69
7.95
8.01
7.88
7.91
                                74

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    Table 29.   AVERAGE SOIL ATMOSPHERE COMPOSITION (PERCENT BY VOLUME)  OF EXPERIMENTAL FEEDLOT SITE
Ui
„ , . Treatment Number
Sampling
depth Gas
(cm) 1234
45 00
2
N2 Cl
co2 Io
«4
Total
91 02
N2
co2
ffl4
3.0

87.2
ay San
™ 9.0
0.8
100.0
4.0
90.2
5.6
0.1
2.8

A 73-1 n
d Cla
15.9 10!
8.2
100.0
3.8
72.9
16.1
7.2
3.1

86.0 _
y San
^ 8.8
2.0
99.9
4.4
88.8
6.5
0.3
2.5

73.8
id
13.2
10.5
100.0
2.4
85.8
8.9
2.9
                 Total
99.9
100.0
100.0
100.0

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NEBRASKA

Physicaj^ Properties  of Soil Sores

In  a  laboratory experiment with  four undisturbed soil cores from a
feedlot, average  infiltration was  1.42 x  10  2  cm/day  (.55 x 10~2 in/
day)  or about  5 cm/yr (2 in/yr).   In one  core, having the slowest
infiltration,  1.5 cm (.6 in.) entered in 1 year and only 2 cm  C-S in}
in  540 days  (27).

Physical characteristics were determined  on  six undisturbed feedlot
cores from a Platte  River valley site near Central City, Nebraska.
The undisturbed cores encased in plastic  (28)  were segmented  into
sections 10 cm long  (3.9 in.).  The change in physical characteristics
of  soil caused by cattle in the  feedlot was  very pronounced and was
limited to the top 15 to 20 cm (5.9 to 7.9 in.) of surface.  Mixing of
soil  and organic  matter occurred above and below an interface boundary.
The most significant physical characteristic of soil profile  in the
beef  cattle feedlot was the interface zone between the organic and
inorganic layer.  The interface  zone is defined as the interface
boundary between  organic matter  and mineral  soil, including about
2 cm  (.8 in.) above and 8 to 10 cm  (3.2 to 3.9  in} below the boundary.
This  layer influenced the movement of water, air, and nutrients in the
soil profile and  into the groundwater.

Bulk  density of the  soil was 1.70 to 1.80 g/cm3 (.06 to .065  Ib/cu. in}
in  the interface  section below the boundary.   The bulk density of
sections below the interface decreased to 1.4  g/cm3 (.05 Ib/cu. in}
which was comparable to that of  cropland.   Average bulk density of the
organic surface section was about 1.0 g/cm3  (.036 Ib/cu. in}.

Organic carbon content was 9.3%  in the manure  surface layer and 2.4%
in  the interface  layer.   Ten centimeters  (3.9  in} below the interface
layer, the organic carbon content of soil was  1.2%, which was about
the same as in the soil of the surrounding cropland.  The particle
density of the manure surface layer was 2.35 g/cm3 (,085 Ib/cu  in.)
which was much lower than 2.68 g/cm3 (.096 Ib/cu. in} for mineral soil.
Air permeability of the feedlot  surface and  interface sections was 1.53
and 0.74 microns2 respectively,  and it increased to 12.8 microns2 in the
section below.   Intrinsic water permeability for the same layers was
0.030 and 0.029 microns2,  and it increased to  0.51 microns2 in the soil
section below.

The high,  organic-matter content in the surface and interface sections
caused a very gradual decrease in water content with increasing suc-
tion up to 0.67 bar  (9.7 Ib/sq.   in}.   Large pores were absent and the
small pores were responsible for low conductivity of water through the
                                  76

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 profile.  Moisture release characteristics were different on disturbed
 samples of the same material.  The change in pore volume and pore size
 distribution of disturbed material from the surface and interface
 sections caused a much greater change in water content over the same
 range of section than in the undisturbed sample.  It is important when
 measuring physical characteristics of animal waste to use the correct
 sampling techniques and the right kind of sample.

 Soil-core, bulk-density patterns did not show a trend attributable to
 feedlots.  Some feedlot locations, compared with the adjacent cropland,
 showed a higher bulk density for the first 2.4 m (2.6 yd).   Average
 bulk densities for the feedlot cores were 1.09 g/cm3 (.04 Ib/cu.  in.)
 for the silt loam and 1.79 g/cm3 (.065 Ib/cu.  inO for the fine sandy
 loam soils.  The manure in the mounds had a bulk density range of
 0.65 to 0.97 g/cm3 (.02 to .035 Ib/cu. in);  however, bulk density
 generally increased with depth, indicating compaction,  continued
 decomposition, and consolidation of the manure material (29,  30).

 The water content in the feedlot soil profile  was fairly uniform with
 profile depth.   The feedlot surface tends to reduce  water infiltration;
 however,  results  suggest a relatively stable  soil-water condition with
 limited water entry into the profile and no  well-defined wetting  fronts.
 The profile beneath the mounds was generally drier than the  surround-
 ing feedlot profiles,  which indicates a lower  water  intake.

 Chemical  Properties of Soil Cores

 Sloping,  Upland Feedlots

 The sloping  feedlots were  found to accumulate  nitrate in the upper
 9.1 m  (9.6 yd)  of the  soil  profile (Figure 15).  There  is approximate-
 ly  34.0 and  8.1 metric tons/ha. (15.2  and 7,4 tons/acre)  more total N
 in  the  feedlot  profile than in the  cropland  (corn) and  abandoned feed-
 lot profiles,  respectively  (Table 30), part  of which can be converted
 to  nitrate.

 The nitrate remains in the  upper  1.5  m (1.6 yd) of the profile, with
 most of the nitrate located on the  lot surface  (Figure  15).  Water
 samples were  obtained  from  43  core  sites and 9  (21%) were above 10 ppm
 N03-N.  The mean N03-N concentration  was 7.2 ppm.  The highest concen-
 trations above  10 ppm  were  generally  flat, upland feedlot sites with
 a water table at  less  than  6.1 m  (6.7 yd).

 Flat Feedlots

 The  flat feedlots were located on the Platte River floodplain on
 sandy-textured soil.  The soil type resulted in 32.5 metric tons/ha.
 (14.5 ton/acre)  total N, lower than observed under the other feedlot
condition (Table 30).

                                   77

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                                     Or
VJ
00
                                                                	  UPLAND FEEDLOTS, 59 cores
                                                                o-o  FEEDLOTS, RIVER VALLEY, 28 cores
                                                                *—•  UNDER MOUNDS> 10 cores
                                                                	  ABANDONED FEEDLOTS, 6 cores
                                                          40
BO
                                                          NO>N, ppm
                   Figure 15.  Average nitrate distribution values in the  profiles  of sloping-
                                          upland, flat  manure mounds and  abandoned  feedlots

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 Table 30.  AVERAGE QUANTITY OF NUTRIENTS IN A 9.1 m PROFILE UNDER THE

            DIFFERENT FEEDLOT AND CROP MANAGEMENT SYSTEMS INVESTIGATED.

                               (kg/ha.)

Sloping or upland
feedlots
Profile under mounds
Flat (river basin)
feedlots
Abandoned feedlots
Crop feedlot rotation
Corn
Alfalfa
Grassland
No. of
profiles
59
10
28
6
5
10
3
8
Nutrients
Total
nitrogen
76,100
54,000
21,300
68,100
47,900
42,000
42,000
18,000
accumulated
NHlf+-N
3,740
6,840
1,900
716
347
319
403
224
to 9.1
N03~-N
1,840
502
627
7,200
2,090
1,100
403
224
The 630 kg/ha. (562  Ib/acre) N03-N was  one of the lowest quantities
observed  for  feedlots,  with only the mound having less N03-N (Table
30) .   Only  5% (1  of 20)  of the water samples from the flat feedlots
contained in  excess of  10  ppm N03-N.   The highest N03-N concentration
detected  in the water samples was 23 ppm, with a mean of only 4.2 ppm.

Mounds

The mounds  are one  way  in  which a feeder can temporarily stockpile and
store  animal  wastes  deposited on the feedlot, and large quantities of
nitrogen  are  stored in  this manner.  In the feedlots cored in this
study, 394  and 170  metric  tons/ha.(175 and 75.8 tons/acre)  Kjeldahl N
and NH^-N were found in  the average 4.0-m (4.4 yd)  depth of mound.

In the soil profile  under  the mounds, only 53.8 metric tons/ha. (24
tons/acre)  Kjeldahl N was  found in 9.1 m (10 yd)  profile.   This
quantity was  22.4 metric tons/ha.(10 tons/acre)  less than the upland
feedlots.    The 9.1 m (10 yd)  profiles under mounds  contained the
largest quantity of NH^-N  found in the cores, with  6.7 metric tons/ha.
(3 tons/acre).  None of the water-table samples contained in excess
of 10 ppm N03-N,
                                  79

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Abandoned Feedlots

The abandoned feedlots contained more NOs-N in the profile than any
other condition studied (Figure 14).  In a 9.1 m (10 yd) profile,
there was 7.2 metric tons/ha.(3.2 ton/acre) of N03-N.  This was almost
3.5 times the quantity of N03-N accumulated under any other feedlot
management system (Table 30).

Abandoned feedlot management appears to be an important consideration
in the accumulation of N03-N in a soil profile.  One abandoned site
accumulated 19.4 metric tons/ha. (8.7 tons/acre) of N03-N in the 7.6~m
(8.3 yd) profile.  Feedlots which were abandoned and then cropped
showed some decrease in N03-N levels throughout the profile; however,
variability within a single lot is too great to draw conclusions.

Two of three (67%) of the water samples had N03-N concentration greater
than 10 ppm.  The average N03-N concentration for the water samples was
40.6 ppm, with a high of 77.2 and a low of 0.6 ppm.

Feedlot-Cropland

Five sites cored were used for cattle feeding.  The feedlot-cropland
rotation has N03-N buildup characteristics intermediate between these
kinds of land use.  There are large quantities of N03-N in the first
2.4 m (2.6 yd) of the soil profile and a large percentage of the cores
to 9.4 m (10.3 yd) have more than 10 ppm N03-N.

The 2.1 metric tons/ha. (.94 tons/acre) N03-N found in a 7.6-m  (8.3 yd)
profile is more than in the feedlot but less than the abandoned feed-
lots.  The NHifN levels were low compared with feedlots and comparable
to the cropland NH4-N  levels.  There was an  increase in Kjeldahl N of
5.9 metric tons/ha.(2.6 tons/acre) over the  corn and alfalfa but 28.2
metric tons/ha.(12.6 tons/acre) less than the  feedlot.  The nitrogen
data indicate that there is an increase in the N03-N levels in the
soil, which has not been utilized by the crops during the summer.  The
maximum, mean, and low N03-N concentrations  in groundwater samples
were 19.1, 13.4, and 9.7 ppm, respectively.  Two of  three samples
(67%) contained N03-N  in excess of  10 ppm.
                                  80

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                               SECTION IX

           INVESTIGATIONS  ON METHODS  OF EXTRACTION  OF NITRATE

              FROM THE  SOIL PROFILES  OF ABANDONED FEEDLOTS

NEBRASKA

Introduction

When  feedlots  are abandoned,  large quantities  of nitrogen  remain that
are readily convertible to nitrate.   Even  if the manure  layer  is
removed, quantities  of nitrogen  in the form of ammonium  and organic
nitrogen remain  in the upper  portion of the feedlot soil profile.  As
oxygen becomes available  to the  soil profile,  these compounds  can be
converted  microbially  to  nitrate.

Recent soil-coring studies by Mielke and Ellis (31) have shown nitrate
concentrations beneath abandoned feedlots  may become quite high.  In
the abandoned  feedlots sampled,  the  average quantity of nitrate-
nitrogen in the  9.1-m  (10 yd)  profile was  7,202 kg/ha.(6424 Ib/acre).
These nitrates at the  deeper  depths  have moved below the plant root
zone and may eventually leach to the water table.  Water samples
obtained from  the groundwater below  the  abandoned  feedlots (32)
ranged from 0.6  to 77.3 ppm N03-N (average 40.5 ppm).

Obviously, there  is  a  need to limit  or stop the movement of nitrate
from abandoned feedlots.  This task  might  be accomplished by estab-
lishing a  high-nitrate-requiring and/or  deep-rooted crop on the
feedlot area when it is abandoned.

Objectives and Methods

The purpose of this  study was  to establish crops which will extract
the nitrates from the  soil profile on  the  abandoned feedlot.    Because
salt concentrations  are high  at  the  feedlot surface, provisions were
made by surface material  removal and crop  selection.

In the spring of  1972, a  portion of  a  feedlot was  abandoned and used
as the experimental  site.  A  total of  12 plots, 4.2 x 6.1 m (5 x 6.7
yd) each, with 0.6 m (.66 yd) wide borders, was established.    The
randomized plot diagram and treatments are shown in Figure 16.
Fifteen centimeters  (5.9  in)  of material were removed from plots 2,  4,
and 6 and replaced with topsoil  from adjacent farmland.  The topsoil-
addition treatment was included  to alleviate any possible salt
problems.  The plots were seeded with  alfalfa and  corn in May,  1972.
These crops have moderate-to-good salt tolerance and will remove
                                 81

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                    I- CORN  SOIL  REMOVED


                    2-ALFALFA  SOIL REMOVED

                    3-CONTROL SOIL  REMOVED
4-CONTROL

5-CORN

6-ALFALFA
00
ro
                                           6
                      Figure 16.  Experimental plot  layout on abandoned feedlot.

-------
nitrates  from  the  soil profile.  Duplicate soil  cores were taken to
3.0 m  (3.3 yd)  from  each plot prior  to planting  and after harvest in
the fall  to  assess the nutrient  status of the soil profile.  These
cores  were analyzed  for ammonia, nitrate, nitrite, phosphorus, and
cations at 0.3 m  (-33 yd)  increments of depth.   Plant samples and
yields were  taken  to determine the amount of nitrogen removed from the
soil profile.

Results

Crop yields  and nitrogen uptake  for  the 1972 and 1973 cropping seasons
are shown in Table 31.  The data show that the nitrogen uptake of the
corn in 1972 was significantly higher than that  of the alfalfa; how-
ever,  after  the alfalfa becomes  established, its nitrogen uptake is
greater than that  of the corn.   Nitrate analysis of the plant material
showed that  the nitrate levels of the corn were  2,230 and 7,423 ppm for
N03-N  in  the stalk.

Table  31.  YIELDS  AND NITROGEN UPTAKE OF THE ALFALFA AND CORN ON
           AN  ABANDONED FEEDLOT
                      Forage yield       Grain yield    Nitrogen uptake
     Treatment       (metric tons/ha.)      (hl/ha.)         (kg/ha.)

                      1972     1973      1972   1973      1972    1973

Alfalfa                ~~                             ~~~
	                   a         b
   Feedlot surface    5.15     16.76                       110     441
   Soil removed       3.83     13.37                        84     348

Corn Forage
   Feedlot surface    7.53     11.31                        98     150

   Soil removed       9.12      6.94                       108      93

Corn Grain
Feedlot surface
Soil removed
65.8
73.0
96.7
71.9
72
78
128
95
 Total of 2 alfalfa cuttings in 1972 (year established).

bTotal of 4 alfalfa cuttings in 1973.
                                  83

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                               SECTION X

                          AIRBORNE POLLUTANTS

INTRODUCTION

Hutchinson and Viets (33) showed that volatilization of NH3 from beef
cattle feedlots contributed significant quantities of NH3 to the
atmosphere and potentially to surface waters.  Their data indicated a
lake in the vicinity of a large feedlot absorbed enough NH3 per year
to raise its N content 0.6 ppm.

While NH3 would seem to be the principal form of N volatilized from a
feedlot, there is a possibility other forms of N, such as volatile
amines and heterocyclic compounds, also could contribute significant
quantities of N to.the air and, subsequently, to surface waters.
These compounds are not only odorous but also offer a metabolizable
substrate readily absorbed by water.  Laboratory and confinement-unit
studies indicate volatile N-containing compounds emanate from, or are
contained in, manure.   'Merkel, Hazen, and Miner (34) found amines in
the atmosphere of a swine confinement unit.  Aliphatic amines were
detected in incubated chicken manure (35).   Burnett (36) showed indole
and skatole, among other components, contributed to the odor of
chicken manure.  Deibel (37) also found indole to be an odor component
of chicken manure.  Since volatile N-containing compounds are found in
chicken and swine manure, some or all of these compounds probably
volatilize from cattle manure, along with NH3, and contribute to odor.

NEBRASKA

Volatilization of Ammonia and Basic N Compounds

Ammonia and basic compounds, such as amine, were trapped in acid.  The
traps were constructed as described by Hutchinson and Viets (33) and
were placed around a small feedlot at the Central City site, in and
adjacent to a cattle pasture, and on cropland at the Treynor, Iowa,
site.  The traps, fabricated of wire mesh with a conical metal roof
and a plywood floor, were placed 1.5 m (1.6 yd) above the ground on
posts.  Each trap contained a 750-ml (45.8 cu. inj) plastic dish filled
with 0.01 h[ H2SOI+.  The trapping solution usually was changed every 1
to 3 weeks during the year, depending on the evaporation rate.

Two traps containing 0.02 N Na2C03 were included at the Central City
site on the east and west ends of the feedlot fence.  These solutions
were tested for total N,  Because of the alkalinity of this solution,
any N present would be due to dust contamination.  This measurement
determines whether the N present in the acid-trap solution reflects


                                 84

-------
 absorption of volatile N compounds and/or dust contamination.

 The acid-trap solutions were assayed for distillable N by steam distil-
 lation with MgO into boric acid and titrated with dilute H2S04 (38).
 Total N was measured in the sample by H2SOt+ digestion and steam distil-
 lation with NaOH into boric acid and titration (39).   Results  showed
 amines and basic N-containing compounds  were probably absorbed in the
 trapping solution along with NH3.   Because some of these N-containing
 compounds, probably short-chain amines,  would distill and titrate as
 NH3,  the steam distillation value  obtained here is called distillable
 N rather than NH3-N.   The distillable-N  value is subtracted from the
 total N value and called nondistillable  N.

 The method described by Ekladius and King (40)  was used to test for
 aliphatic amines.

 Average values for distillable  N absorbed by the three traps around
 the feedlot and by two traps in the  surrounding cropland are plotted
 in Figure 17.

 Distillable-N evolution from the feedlot was variable.   No livestock
 were  in the feedlot  until  the first  part of October.   Periods  of
 appreciable precipitation  during the fall  sampling period were followed
 by an increase in  distillable-N evolution.   The high  distillable  N the
 first part of August  coincided  with  rain and manure-mounding.   This
 peak  was  much higher  than  later peaks preceded  by  precipitation,  so it
 was assumed the surface disturbance  caused  by mounding increased  the
 quantities of distillable  N  being  released.   Mounding is  practiced in
 this  area as  a method of on-site manure  disposal  and  to provide  a dry
 area  for  the  animals.   Distillable-N evolution  increased  greatly  in
 October when  animals  were  placed in  the  feedlot  and rain  wet the
 feedlot  (Figure 17).   As cold weather set  in  and precipitation
 decreased,  distillable-N evolution decreased.   The spring was  extremely
 dry and distillable-N evolution  did  not  generally  increase with warming
 weather until  late March.  Distillable-N evolution increased in late
 March and early April  even though the cattle were  taken from the  lot
 in  April  and precipitation was  limited.  The  increase  in  distillable
 N trapped  at  the feedlot and  controls during this period  coincided with
 application of anhydrous NH3  to  adjacent cornfields.  However,  other
 factors probably enter  into the  distillable-N increase in the  spring.

 Throughout the year,  distillable N trapped at the feedlot site was much
 greater than that trapped  in  the cropland.  The yearly average values
were  148 kg/ha.  (132  Ib/acre) per year for the feedlot and 16 kg/ha.
 C14 Ib/acre) per year for the cropland, a significant difference at
 the 5% level as determined with the F test.
                                 85

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00
                             500
                             450
                            4OO
                             350
                             300
                             250
                             200
                              (30
                              100
                                                                                (563)
 CATTLE NUMBERS


	107-
                                                                               W-H\"H
                                  JUL  AUG  SEPT  OCT   NOV  DEC   JAN  FEB   MAR
                                                    TIME, months
               Figure 17.  Distillable N absorption from the  air  around a small feedlot  and
                                     adjacent cropland at Central  City,  Nebraska.

-------
 Figure  18  shows  nondistillable N  from the  traps  around the  feedlot  and
 the  cropland.  Obviously,  significant quantities of N other than
 NH3-N came from  the  feedlot.  For the short period, the  feedlot aver-
 aged 21  kg/ha. C18.7  lb/acre)/yr nondistillable N, while  the cropland
 averaged 3.3  kg/ha.(2.9  lb/acre)/yr which  was significantly different
 at the  5%  level.   For the  same period,  distillable-N evolution was
 218  and  23.6  kg/ha. (194  and  21 lb/acre)/yr for the feedlot  and crop-
 land, respectively.  Total-N values from the traps filled with
 Na2C03  during the  same period were 1  kg/ha.  (-89 lb/acre)/yr or less,
 so the values obtained from  the acid  traps should represent basic
 volatile-N compounds and not N from dust contamination (7).

 The  results obtained from  the cattle  pasture and cropland at Treynor,
 Iowa, (Site 2) are shown in  Figure 19.  The values obtained from July
 through  November were tested with the F test, and the pasture area was
 significantly different  from the  cropland  at the 5% level.  To the
 middle of  November, distillable N trapped  around the pasture was
 significantly greater than that trapped from cropland.   In  the latter
 part of  November,  the cattle were taken off the  pasture  and put on the
 cropland corn stubble.   Consequently,  from late  November to late
 February,  greater  amounts  of distillable N were  trapped  from the crop-
 land than  from the pasture.  For  the  year, distillable-N evolution
 averaged 15 kg/ha. (13.4 lb/acre)/yr  from  the pasture and 11 kg/ha.
 C9.8 lb/acre)/yr from the  cropland.   The distillable-N values in this
 case probably represent  NH3 almost exclusively.   For the pasture,  the
 value for  nondistillable N was 0.45 kg/ha. (.4 lb/acre)/yr  and for the
 cropland was  0.30  kg/ha. (.27 lb/acre)/yr  (7).

 COLORADO

 Significance  of Ammonia  to Plants

 Monitoring the disappearance of NH3 from an airstream flowing through
 a small  growth chamber containing  a single corn,  soybean, cotton,  or
 sunflower seedling about 15 to 25  cm  (5.9  to 9.9 in^  tall indicated
 that plant leaves absorb significant quantities  of NH3 from the air,
 even at  naturally-occurring,  low-atmospheric, NH3 concentrations.

Measured NH3 absorption rates showed  large diurnal fluctuations and
 varied somewhat among species,  but differed little with the nitrogen
 fertility  level of plants within  a species.  The  data indicate that a
 field crop growing in air  containing NH3 at normal atmospheric concen-
 trations might satisfy as much as  10 to 20 percent of its total N
 requirement by direct absorption of NH3 from the  air.   In areas where
 the atmosphere has been enriched with NH3 volatilized from  cattle  feed-
 lot surfaces,  this fraction might be even higher.
                                87

-------
00
oo
in
o
o
CK
I-  I.
—  >»
2  X
                             40
                              30
                        Ul X
                        -i S
                        CD
                         U)

                         o
     20
                              10
                                                FEEDLOT
                                                              ONTROL
                                   MAR    APR    MAY     JUN

                                         TIME,  months
                         Figure 18.  Nondistiliable N  absorbed by the  trapping
                                      solution at Central City, Nebraska.

-------
                                                CATTLE  NUMBERS
oo
V£>
                        JUL   AU6   SEPT
OCT   NOV   DEC
  TIME, months
JAN   FEB   MAR   APR   MAY   JUN
                   Figure  19.   Distillable N volatilized from pastured cattle
                                      and cropland near Treynor, Iowa.

-------
Foliar C02 and NH3 uptake rates measured in a typical 24-hour experi-
ment are shown in Figure 20.  Details of the experimental procedures
used in the experiments are described by Hutchinson (41).  The NH3
absorption rate shown in Figure 20 was relatively constant during the
first day, but dropped sharply at the beginning of the dark period,
apparently reflecting the closing of the stomata.  It is important to
realize that, since the mass flow of NH3 into the plant chamber
remained constant, the lower absorption rate at night occurred in the
presence of an NH3 concentration about three times greater than the
day concentration; thus the difference in day and night uptake rates
is even more pronounced than is first apparent in the graph.  Immedi-
ately after the lights were turned on the following morning, the NH3
absorption rate climbed rapidly and after about two hours reached a
plateau slightly higher than that which prevailed the preceding day.
The higher uptake rate on the second day is at least partially
attributable to an overnight increase in the leaf surface area.  The
uptake of C02 followed a pattern similar to that of NH3 except that
the net uptake was, of course, negative during the dark period owing
to the respiratory release of the gas.

The total amount of NH3 absorbed by the soybean during the experiment,
about 70 ng, was nearly enough to saturate the amount of water con-
tained in the plant, if its pH were 6.50.  Therefore, the absence of
any hint of NH3 saturation in Figure 20, along with the strong
dependence of the uptake rate on stomatal opening, lends support to
our contention that the absorbed NH3 was metabolized rather than
simply adsorbed onto exterior leaf surfaces or passively dissolved in
the water bathing leaf mesophyll cells.  Additional evidence is pro-
vided by Porter et_ a^. (42) who found 15N-enriched amides, amino
acids, and proteins in plants previously exposed to labelled gaseous
NH3,

Subsequent experiments were designed to determine whether foliar up-
take of gaseous NH3 was limited primarily by the diffusion rate of
NH3 through air or by some biochemical or biophysical bottleneck
deeper inside plant leaves.  Rates of foliar uptake of gaseous NH3,
net photosynthetic rates,  and transpiration rates of corn and soybean
seedlings were computed from the changes in NH3, C02, and H20 vapor
concentrations of a gas mixture flowing through a plant growth cham-
ber in which a single corn or soybean seedling was growing.  Results
of all the experiments are summarized in Figure 21 where the NH3
uptake rate measured under each set of experimental conditions is
plotted against the diffusion-limited uptake rate predicted by the
following equation for the same set of conditions:  NH3 uptake equals
Ca/ra + rs5 where ca is the NH3 concentration of bulk air outside the
plant leaf, ra is the diffusive resistance to NH3 transport across the
boundary layer surrounding the leaf, and rs is the resistance to
                               90

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                  8
   12        16

Time  (hours)
20
24
Figure 20.  Foliar C02  and NH3  uptake rates of soybean
               (final leaf surface area,  89 cm2).
                         91

-------
diffusion of NH3 through leaf stomata and substomatal  cavities  to the
surface of a leaf mesophyll  cell  wall.   The equation was  derived from
the general gas diffusion equation based on the resistance model first
advanced by Gasstra (43) by  applying a series of arguments leading to
the conclusion that both the leaf mesophyll resistance to NH3 dif-
fusion and the NH3 concentration  in plant cell fluids  are negligible
(41).   The total of the two  resistance terms in the above equation
was estimated for each set of experimental conditions  from transpira-
tion,  H20 vapor concentration, and temperature data by assuming that
air adjacent to mesophyll cell wall surfaces is saturated with
respect to H20 vapor, and that identical geometrical limitations are
imposed upon the diffusion both NH3 and H20 vapor as they move, albeit
in opposite directions, between wet mesophyll cell wall surfaces and
bulk air outside the plant leaves.

Figure 21 includes data for two different crop species and for exper-
iments conducted under a wide range of environmental conditions.  The
ranges of environmental variables represented by data points_in the
graph were:  atmospheric NH3  concentration,  150 to  1530 ug m   ;
atmospheric C02 concentration,  50 to 540 ppm  (v/v); air  temperature,
18.7 to  32.9°  C; and incident light energy,  0.3 to  0.7 cal cm   min.
All the  data points fall very close to the  line rising diagonally  from
the origin with slope  equal to one,  indicating that the NH3 uptake
rates measured experimentally were nearly  identical to those theoret-
ically  expected if the uptake were diffusion-limited.  On the  average,
predicted NH3  uptake rates were  only  about  two percent lower than
measured ones.  The  conclusion drawn  from  Figure  21 is that  the
observed differences  among NH3 uptake rates induced by modifying_the
atmospheric  C02 or NH3 concentration,  air  temperature, or light inten-
sity were manifestations  only of the  effect of these  variables on the
effective  cross-sectional area available for diffusion represented by
the sum of  the areas  of stomatal aperatures.  Apparently, then, the
wet surfaces  of corn and soybean mesophyll cell walls behaved as
 infinite sinks for atmospheric NH3 over the range of  concentrations
 studies, and foliar NH3 uptake was limited only by the time  required
 for gaseous  NH3 molecules to diffuse from external air through the
 stomata to a wet, cell wall surface.

 The importance of atmospheric NH3 as an agent for the transport and
 redistribution of N both within and among ecosystems  has been^vastly
 underestimated.  Cattle feedlots are apparently one of the major
 sources of NH3 in the atmosphere.  Research has shown that a  signif-
 icant amount of the NH3 volatilized from the surface of  cattle feed-
 lots is absorbed by soil and water surfaces in the vicinity of the
 feedlots.  The data invalidate the concept  that only runoff and deep
 percolation from  cattle feedlots require control to prevent N
 enrichment of the surrounding environment.  Although control  of runoff
                                  92

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               30      60       90       120
                Measured NH3 Uptake ( f*.g dm"zhr~')
150
Figure 21.  NH3 uptake rates predicted by equation  C /r  +
            vs. NH3  uptake rates measured experimentally.
            The diagonal line through the graph  represents
                   all  points with equal coordinates.
                            93

-------
into streams to prevent pollution by sediment, phosphorus, and organic
wastes justifies adequate and often expensive design of feedlot instal-
lations, N pollution may still occur.
Calculations based on the data in Figure 20 indicate that annual
absorption by plant canopies growing in air containing NH3 at normal
atmospheric concentrations could be about 20 kg per hectare.  This rate
of NH3 supply is large enough to contribute significantly to the N
budget of a growing plant community and could exert a prodigious
influence on the long-term behavior of an ecosystem.  Near cattle feed-
lots where the atmosphere is enriched with feedlot volatiles, foliar
NH3 absorption is probably even higher.  Our data, together with data
on the absorption of atmospheric S02 C44) and 03 (45) by plant leaves,
also suggest an important role for green vegetation in the decontam-
ination of the earth's atmosphere.

Identification of Aliphatic Amines from Cattle Feedlot Volatiles and
the Effect of these Compounds on CktolMa.
Studies were initiated to determine if appreciable quantities of
volatile N-materials other than ammonia are evolved from cattle feed-
yards, to illucidate their chemical composition to determine their
effect on aquatic organisms.

Seven aliphatic amines have been identified and the presence of other
higher molecular weight N- compounds are suspected.  The materials
identified and their concentrations relative to ammonia are shown in
Table 32 (46).  These seven compounds are estimated to comprise about
five percent of the nitrogen volatilized from a cattle feedyard.

Efforts to separate these nitrogen volatiles from ammonia and to
identify them led to the development of a new gas chroma tographic (GC)
technique for the separation and characterization of aliphatic amines
and the revision of a method in which derivatives of aqueous solutions
of amines could be prepared for confirmatory analysis.  The new GC
system (47) involved injection of aqueous sample5 of amine hydrogen
sulfate salts onto an Ascarite precolumn in a GC inlet chamber and
subsequent separation of the different amines on specific types of GC
columns.  This method was also adapted to the analysis of aliphatic
N-nitrosamines (48) .  The new amine derivative procedure involved the
preparation of stable pentafluorobenzamide compounds from penta-
f luorobenzoyl chloride and aliphatic amines in aqueous solution (46) .

As appreciable amounts of nonammonia volatile nitrogen were shown to
evolve from cattle feedyards, work was initiated to determine if the
aliphatic amines were biologically active in the surface waters which
can collect them.  CkloleMa e£icp6 o-Ldna was selected as the test
                                  94

-------
 Table 32.   ALIPHATIC AMINES IDENTIFIED AS FEEDLOT VOLATILES AND
                 THEIR CONCENTRATIONS RELATIVE TO AMMONIA
                                             Concentration as
     Amine                                       of Ammonia
 Methyl  amine                                        1.0

 Dimethyl  amine                                       0.5

 Ethyl amine                                          2.0

 d-propyl  amine                                       0.5

 >c4o-propyl amine                                     1.0

 n-butyl amine                                        0.1

 n-amyl  amine                                        0.1


 organism.  Studies were  initiated to determine  if  the  amines  affect  the
 alga in pure culture.  The initial studies showed  that the  amines
 affect algal population  growth.  A 50 percent reduction in  algal popu-
 lation growth, PI ,2, was detected at amine concentrations ranging  from
 1.2 to  143 ppm amine-N (Table 33).  Subtoxic amine concentrations
 stimulated algal growth  (Figure 22).  Primary amines were more
 inhibitory than -c40-, 4ec-, and dialkyl amines  (49).   The source of
 inorganic N, ammonium or nitrate, had little effect  on P^ values of
 the normal primary amines and  dimethyl amine.  However,^initial N
 source did affect the toxicity of the branched primary amines and
 diethyl amine.  Apparently the configuration of the  amine is  important
 in its inhibition of the alga's metabolism.  It was  also found that
 the alga could not utilize amine-N for growth, with  or without an added
N source.

To attempt to illucidate the mechanism(s) by which amines affect C.
eJULip&oMza. metabolism the effect of methyl amine  on the alga's N
metabolism, photosynthesis, and respiration was investigated.  Methyl
amine accelerated ammonium assimilation (Figure 23) but  did not affect
short-term nitrate uptake (apparently nitrate reduction  is the rate-
 limiting step in nitrate assimilation).   A Lineweaver-Burke treatment
of ammonium uptake data  (Figure 23)  shows that methyl  amine was not
competing with ammonium for the site of enzymatic  ammonium assimilation.
                                  95

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Table 33.  STATISTICS RELATING ALGAL POPULATION TO AMINE CONCENTRATION
Nitrogen
Amine Source^


Methyl NO ~
O
NH4+
Dimethyl NO,"
NH/
4

Ethyl NO "
NH/
4
Die thy 1 NO "
o
.
NH4

n-Propyl N0~
NH/
tso-Propyl NO-"
NH4+

n- Butyl N03~
NH/
4

seo-Butyl NO,"
O
NH/
4
Regression
Equation

A
log y =
log y =
log y =
A
log y =
A
log y =
log y =
log y =
A
log y =
A
log y =
log y =
log y =
A
log y =
A
log y =
A
log y =
A
log y =
A
log y =


3.42-0.256x
3.39-0.072x
3.49-O.Olx
3.27-O.OOSx

3.30-0.006x
3.49-0.007X
3.49-O.OOSx

3.27-0.008x

3.54-0.005x
3.57-0.005x
3.48-0.002X
3.50-0.014x

3.45-O.OOSx
3.42-O.Ollx

3.47-0.003x
3.50-0.004x
Correlation
Coefficient


0.997
0.881
0.995
0.988

0.985
0.954
0.972

0.989

0.988
0.966
0.970
0.971

0.888
0.971

0.945
0.939
>,b
ppm

1.2
4.2
31.7
36.3

48.6
41.2
120.4

36.7

60.2
59.1
142.9
187.6

59.04
27.36

120.4
77.7
  Cells were cultured in a nutrient solution containing either nitrate
  or ammonium.

  Concentration of amine which reduces the alga population growth by
  one half.
                                   96

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                     _L
                                      ETHYL  AMINE
                                     j	I	•	1	
               10
 20    30    40     50    60
AMINE-N  CONCENTRATION (ppm)
                                                     70
Figure 22,   Effect of amine  concentration  on C. ellipsoi-dea
                         population  growth.
                            97

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vo
00
  O.I I

  o.io

^ 0.09
.c

z 0.08
e
> 0.07

  0,06

  0.05

   0.04
                                 0.001
                                                                        y= 0.0863 + (0.387 )X
                                                                        r = 0.968
                                                                        y = 0.0549 + (0.454 )X
                                                                        r = 0.804
                            0.005            0.01
                                       1/C (1/ppm  NH*-N)
                                                                                               0.02
                            Figure 23.   Effect of methyl  amine on C. elli-psoidea
                                                    airanonium-N uptake.

-------
 Methyl amine also affected the alga's photosynthetic and respiratory
 processes.   Methyl amine concentrations of 2.5 ppm or less  stimulated
 oxygen production (Figure 24).  The oxygen concentrations shown are
 apparent oxygen levels;  correction was made for temperature,  pressure,
 and solution phase oxygen, but not for respiratory consumption.   With
 more than 2.5 ppm of methyl amine, oxygen production decreased rapidly
 with the increase in amine concentration.   Algal oxygen production was
 decreased by one-half at about 9 ppm amine-N.   The amine also stimu-
 lated the respiratory consumption of oxygen.   During the 4-hour incu-
 bation period with no amine added, 0.65 ml of  oxygen was consumed
 (Figure 25).

 Aliphatic amines  have been shown to inhibit isolated plant  chloroplast
 photophosphorylation (ATP synthesis).   Even very high concentrations
 of methyl amine (500 ppm)  did  not inhibit  photosynthetic ATP  synthe-
 sis in intact C.  eJttipA04,d&a cells.   Apparently,  aliphatic  amines
 affect the metabolism of isolated chloroplasts  and algal cells
 differently.

 Chemical equilibria provide a  method for describing the physical  and
 chemical behavior of aliphatic amines  and  ammonia in aqueous  systems.
 Close inspection  of chemical equilibrium of gaseous amines  with  aqueous
 surfaces suggests that volatile aliphatic  amines  from the atmosphere
 are highly capable of concentration  into aqueous  systems.   These  calcu-
 lations  demonstrate that  amines  can  concentrate  in surface  waters from
 the atmosphere.   Analysis  of lake waters located  near a large  cattle
 feedlot  showed seasonal  fluctuations  in amine and ammonia concentra-
 tions,  but no large accumulation (Table 34).  The compounds may be
 metabolized by microorganisms  or adsorbed  by lake sediment.

 To  determine  if there  are  organisms which  decompose aliphatic  amines
 present  in surface waters  and  sediment,  samples of lake  sediment  and
 water were incubated  in  the laboratory  with methyl  and  dimethyl amines.
 Both  amines were  readily  degraded, with methyl amine  being  degraded
 more  rapidly  than dimethyl  amine.

 The organisms  in  lake  water and  sediments may account for the  lack of
 an  accumulation of amines  in such  waters located  near cattle feedyards.
 Apparently, microorganisms  rapidly metabolize the  amine-N,  thus enter-
 ing this N into the N  cycle of the aquatic system.  This idea  is  sup-
ported by the  concentrations of  amines measured by periodically
 analyzing lake waters  during the  year  (Table 34).   During cold weather
 (periods of low microbial  activity), amine concentrations were highest.
The amine concentrations decreased as the seasonal  temperatures
 increased.
                                  99

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           1.2  T
          0.9
                            STANDARD ERROR
                    5      10     15     20    25
                   METHYL AMINE CONCENTRATION
                         (ppm AMINE- N)
Figure  24.   Effect of methyl  amine on  C.  ellipsoidsa
                   photosynthetic CL production.
                           100

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      0-61
_L
        J_
                                       J_
        05       10      15      20
              METHYL  AMINE CONCENTRATION
                     (ppm  AMINE -N)
                               25
Figure 25.  Effect  of methyl  amine on C. elHpsoi-dea
                  respiratory CL consumption.
                          101

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Table 34.  TOTAL DISTILLABLE N AND ALIPHATIC AMINE CONTENT OF A
                  LAKE LOCATED NEAR A CATTLE FEEDLOT
                                Total Volatile N          Total Amine-N
Date of Sampling                     Cppm)                    (PPm)
3- 2-73b
A
4-19-173a
7- 5-73
8- 8-73
3.7

0.65
e
e
0.183C

0.052
0.018
£
3.
 Located about 2 km east of a 90,000-unit feedlot

 Lake was covered with about 10 cm ice.

cComposed of four identifiable amines:  methyl, 94 ppb; dimethyl,
 41 ppb; ethyl, 46 ppb; and isopropyl, 2 ppb.

 No ice remaining on lake.
Q
 No measurable volatile N.

 No detectable amine.

NEBRASKA

Significance of Sulfur Compounds

Attempts to control odors and gases from beef cattle feedlots and other
beef-confinement areas have been mostly unsuccessful.  Accordingly,
we must take a more basic approach to the problem.  This involves
identification, quantification, and source delineation before control
measures can be devised.  To date, only NHs and presumptive evidence
showing amines are volatilized from beef cattle feedlots have been
reported (7, 33).  Therefore, more work is needed to identify odor
compounds from beef cattle manure and feeding areas.

The purpose of the following studies was to identify and quantify some
of the sulfur compounds and gases emanating from anaerobically incu-
bated bovine manure.  These studies were conducted in anaerobic
                                 102

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 columns and  in  the  feedlots.  The  compounds were measured with  gas
 chromatography.

 Carbon/1 sulfide  (COS)  and hydrogen sulfide were detected above the
 anaerobic manure  (figure  26).  Carbon dioxide, CH^, and 02 were meas-
 ured also  (Figure 27).

 About 0.1 ppb of COS was  detected  in gas samples from caissons beneath
 the solids retention basin of a broad-basin terraced feedlot.  The
 feedlot installation has  been described previously.  The gas was
 detected also from  the  surface of  the basin but not from the liquid
 retention pond.  These  results show COS is produced in the feedlot (50),

 Carbonyl sulfide has not  been reported from manure or feedlots previous-
 ly.  It is present  in natural gas  (51) and in the gases from some vol-
 canoes (52).  The gas is  toxic to  the central nervous system and
 decomposes to H2S CS3).   It is speculated that COS could be an inter-
mediate in the sulfur scheme of bacteria.  It is too early to assess
 the importance of COS in  the feedlot.   Carbonylsulfide may be important
 in closed confinement units; however,  this would depend on the concen-
 trations produced.  Carbonyl sulfide might be a precursor to H2S and
more information is needed on such chemical reactions.

The results also show H2S and COS can be detected in very low concen-
trations which will be useful for management-system assessment.
                                103

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 II

 IO

 9

 8

 7

_6
E
N
             •  COS FRESH MANURE

             o  H2S FRESH MANURE

                    COMPOST
                                      18  20  22  24  26  28  30  32  34  36
4   68   10   12   14
                              TIME, days
Figure 26.  Production of carbonyl sulfide (COS)  and dihydrogen  sulfide
              (H2S) from anaerobically incubated  manure  and  compost.

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•  c
o  c
                                  FRESH MANURE
                                  COMPOST
                                  FRESH MANURE
                               a  COMPOST
                                  FRESH MANURE
                                  COMPOST
                      10  12  14   16  18 20  22 24  26 28  30  32  34  36
                             TIME, days
Figure  27.  Gases present above  anaerobically incubated manure and compost,

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14.  Gilbertson, C. B.,  T. M.  McCalla, J. R.  Ellis,  and W. R. Woods,
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20.  Elliott, L. P.,  T.  M. McCalla, L. N. Mielke, and T. A.  Travis.
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23.  Elliott, L. F.,  T.  M. McCalla, N. P. Swanson,  L.  N. Mielke, and
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25.  Stewart, B. A., F.  G.  Viets,  Jr.,  G.  L. Hutchinson,  W.  D.  Kemper,
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27.  Mielke, L. N.  1974.   Physical characteristics  of the surface and
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28.  Mielke, L, N.  1973.   Encasing undisturbed soil  cores  in plastic.
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29.  Mielke, L. N., and J.  R. Ellis.  1972.  Nebraska feedlot soil
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     p. 134.

30.  Ellis, J. R., L. N. Mielke, and G.  E.  Schuman.   1972.   Nebraska
     feedlot soil coring study.   II. Chemical  findings.   Agron.
     Abstr., p. 131.

31.  Mielke, L. N., and J.  R. Ellis.  1973.  Chemical and physical
     characteristics of soil profiles under abandoned feedlots.   Agron.
     Abstr., p. 126.

32.  Ellis, J. R., L. N. Mielke, and G.  E.  Schuman.   1975.   Nitrogen
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     Sci. Soc. Amer. Proc,  39:48-51.

33.  Hutchinson, G. L.,  and F. G.  Viets, Jr.   1969.   Nitrogen enrich-
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34.  Merkel, J. A., T. E.  Hazen, and J.  R.  Miner.   1969.   Identification
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36.  Burnett, W. E.   1969.  Air pollution from animal wastes:  Deter-
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37.  Deibel, R. H.  1967.  Biological aspects of the animal waste dis-
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41.  Hutchinson, G. L.  1973.  Foliar absorption of atmospheric ammonia.
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42.  Porter, L. K., F. G. Viets, Jr., and G.  L.  Hutchinson.  1972.  Air
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     at low sulfur dioxide concentrations.   Nature 224:1229-31.

45.  Rich, S., P. E. Waggoner, and H. Tomlinson.   1970.  Ozone uptake
     by bean leaves.  Science 169:79-80

46.  Mosier, A. R., C. E. Andre, and F.  G.  Viets,  Jr.  1973.  Identi-
     fication of aliphatic amines volatilized from a cattle feedyard.
     Envrion. Sci. Technol. 7^:642-644.

47.  Andre, C. E., and A. R. Mosier.  1973.   A precolumn inlet system
     for the gas chromatographic analysis of trace quantities of short-
     chain aliphatic  amines.  Analyt. Chem.  45j 1971-3.

48.  Mosier, A. R., and C.  E. Andre.  1973.   Direct gas chromatographic
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     Chem. 45:372.
                                  109

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49.  Hosier, A.  R.   1974.  Effect of cattle feedlot volatiles, aliphatic
     amines on Chlorella ell-Lpso-Ldsa growth.   J.  Environ.  Qual. £:36-38.

50.  Elliott, L. F., and T. A.  Travis.   1973.  Detection of carbonyl
     sulfide and other gases emanating from beef cattle manure.  Soil
     Sci. Soc. Amer. Proc. 57:700-702.

51.  Hegedus, L. L., and I. M.  Whittemore.  1969.  Determination of
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                                  110

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                         LIST OF PUBLICATIONS


 Andre, C. E., and A. R. Mosier.  1973.  A precolumn inlet system for
 the gas chromatographic analysis of trace quantities of shortchain
 aliphatic amines.  Analyt. Chem. 45:1971-1973.

 Burwell, R. E., G. E. Schuman, R. F. Piest, R. G. Spomer, and T. M.
 McCalla.  1974. Quality of water discharged from a diversified agricul-
 tural watershed in southwestern Iowa.   Water Resour. Res. 10:359-365.

 Cross, 0.  E., and C. B. Gilbertson.  1969.  Management and control of
 beef feedlot waste.   Farm, Ranch and Home Quarterly, Nebraska Agr.  Exp.
 Sta., Lincoln, Winter 1969, p. 20-21.

 Duke, H. R., E.  G. Kruse,  and G. L. Hutchinson.  1970.   Automatic Vacu-
 um Lysimeter for Monitoring Percolation Rates.  U.  S.  Dept.  Agr.,
 ARS 41-165, September 1970, 12. p.

 Elliott, L. F.  1972.  Pollution of air, soil  and water by livestock.
 In:  Proceedings,  Livestock Waste Management Research  Review.  Lincoln,
 Nebraska,  (November)   p.  23-28.

 Elliott, L.  F.,  J. A. DeShazer, E.  R.  Peo,  Jr.,T. A. Travis,  and T.  M,
 McCalla.   1974.   Some constituents  in  the atmosphere of a housed swine
 unit.   In:   Proceedings,  International  Livestock  Environment  Symposium.
 Lincoln, Nebraska  (April  1974).  p.  189-194.          ~~	

 Elliott, L.  F.,  and  T.  M.  McCalla.   1971.   Air pollution  from agricul-
 ture.   In:   Exploring Nebraska's  Pollution  Problems.  Proceedings,
 Symposium,  Lincoln, Nebraska  (April  1971).  p.  Cl-6.

 Elliott, L.  F.,  and T.  M.  McCalla.   1972.   The composition of the soil
 atmosphere  beneath a  beef  cattle  feedlot and a cropped  field.  Soil
 Sci. Soc. Amer.  Proc. ^6_:68-70.

 Elliott, L.  F.,  and T.  M.  McCalla.   1973.   The fate of  nitrogen  from
 animal wastes.   In:   Proceedings, Nitrogen  in  Nebraska's Environment
 Conference,  Lincoln,  Nebraska  (April 1973).  p. 86-110.

 Elliott, L.  F.,  T. M. McCalla,  and J. S. Boyce.  1970.  Soil atmosphere
 composition beneath a beef feedlot and cropped field.   Agron. Abstr..
 p.  108.

 Elliott, L. F.,  T. M. McCalla,  J. A. DeShazer  and E. R. Peo, Jr.  1974.
 Bacteria in the  atmosphere of a housed swine unit.  Bact. Proc., p, 6.

 Elliott, L. F.,  T. M. McCalla,  and L. N. Mielke.  1971.   Ammonium,
nitrate, and total nitrogen in  the soil water of a feedlot soil profile.
Bact. Proc., p.  14.

                                  Ill

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 Elliott,  L.  F,,  T.  M.  McCalla,  L. N.  Mielke,  and  T.  A.  Travis.   1972.
 Ammonium, nitrate,  and total  nitrogen in  the  soil water of feedlot  and
 field  soil profiles.   J.  Appl.  Microbiol.  23:810-813.

 Elliott,  L.  F.,  T.  M.  McCalla,  N. P.  Swanson,  L.  N.  Mielke,  and T.  A.
 Travis.   1971.   Soil water nitrate  levels  beneath two  feedlots.  ( Abstr.)
 Invitational  Paper  #71-711, ASAE Winter Meeting,  Chicago,  111.,
 December  1971.

 Elliott,  L..F.,  T,  M.  McCalla,  N..  P.  Swanson,  and  F.  G. Viets,  Jr.
 1971.   Use of caissons for sampling chemical  and  biological  conditions
 beneath a beef feedlot.   ASAE Trans.  1£:1018-1019.

 Elliott,  L.  F.,  T.  M.  McCalla,  N. P.  Swanson,  L.  N.  Mielke,  and T.  A.
 Travis.   1973.   Soil water nitrate  beneath a  broad-basin terraced
 feedlot.  ASAE Trans.  _16:285-286, 293.

 Elliott,  L.  F.,  G.  E.  Schuman,  and  F.  G. Viets, Jr.  1971.   Volatilization
 of nitrogen-containing compounds from beef cattle areas.   Soil  Sci. Soc.
 Amer.  Proc.  56:68-70.

 Elliott,  L.  F.,  and T.  A. Travis.   1972.   Detection  of carbonyl  sulfide
 and  other gases  above  anerobically  incubated  manure.   Agron.  Abstr.,
 p. 95.

 Elliott,  L.  F.,  and T.  A. Travis.   1973.   Methods for  measuring odorous
 emissions from animal  wastes.   Agron.  Abstr.,  p.  172.

 Elliott,  L.  E.,  and T.  A. Travis.   1973.   Detection  of carbonyl  sulfide
 and  other gases  emanating from  beef cattle manure.   Soil Sci. Soc.  Amer.
 Proc.  37_: 700-702.

 Ellis,  J. R.   1972.  Characteristics  of animal waste runoff.  In:
 Proceedings,  Livestock Waste  Management Research  Review, Lincoln,
 Nebraska  (November) .   p.  49-53.

 Ellis,  J. R., L. N. Mielke, and G.  E.  Schuman.  1972.   Nebraska feedlot
 soil coring  study.  II. Chemical findings.  Agron. Abstr., p. 131.

 Ellis,  J. R., L. N. Mielke, and G.  E.  Schuman.  1975.   Nitrogen  status
 beneath beef cattle feedlots  in eastern Nebraska.  Soil  Sci.  Soc. Amer.
 Proc.  39(1):48-51.

 Gilbertson,  C. B., T.  M. McCalla,  J. R. Ellis, and W. R. Woods,   1971.
Methods of removing settleable solids from outdoor beef  cattle feedlot
runoff.  ASAE Trans. 14:899-905.
                                   112

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 Gilbertson, C. B., T.  M. McCalla,  J.  R.  Ellis,  0.  E.  Cross,  and W.  R.
 Woods.   1970.   The effect of animal density and surface slope on char-
 acteristics of runoff, solid wastes and  nitrate movement on  unpaved
 beef feedlots.  Nebraska Agr. Exp. Sta.  Bull. 508.

 Gilbertson, C. B., T.  M. McCalla,  J.  R.  Ellis,  0.  E.  Cross,  and W.  R.
 Woods.   1971.   Runoff, solid wastes,  and nitrate movement on beef feed-
 lots.   J.  Water Poll.  Control Fed. 43:483-493.

 Gilbertson, C. B., T.  M. McCalla,  J.  R.  Ellis,  and W.  R.  Woods.   1972.
 Characteristics of manure accumulations  removed from  outdoor,  unpaved,
 beef cattle feedlots.   In:   Livestock Waste Management and Pollution
 Abatement.  Amer.  Soc. Agricultural Engineers,  St. Joseph, Michigan.
 p.  132-134.

 Gilbertson, C. B., T.  M. McCalla,  and A.  T.  Sobel.  Analyzing physical
 and chemical properties  of solid wastes  from livestock  and poultry.
 ASAE Trans.  (In press)

 Gilbertson,  C.  B., J.  A.  Nienaber,  T. M.  McCalla, J.  R. Ellis,  and W. R.
 Woods.   Beef cattle feedlot runoff, solids  transport  and  settling
 characteristics.   ASAE Trans.  15:1132-1134.

 Gilbertson,  C.  B., J.  A.  Nienaber,  T. M.  McCalla, J.  R. Ellis,  and T. J.
 Klopfenstein.   1973.   Energy and nutritional value of beef cattle feedlot
 waste fractions as affected by ration.  Agron. Abstr., p. 174

 Hinrichs,  D. G.  1973.  Physical properties  of a  Colo  silty clay  loam
 soil during 2  years' irrigation with  effluent from beef feedlots and
 water from a creek.  M.S. Thesis,  University of Nebraska, Lincoln.

 Hinrichs.  D. G., A. P. Mazurak, and N. P. Swanson.  1974.  Effect of
 effluent from  beef feedlots  and the physical and chemical properties of
 soil.  Soil  Sci. Soc.  Amer.  Proc.  J58(4)  :661-663.

Hinrichs,  D. G., A. P. Mazurak, N.  P. Swanson, and L. N. Mielke.  1973.
Effect of  effluent from  beef feedlots on physical properties of soil.
Agron. Abstr.,  p.  124.

Hutchinson,  G.   L.,  R. J. Millington, and D.  B.  Peters.  1972.  Atmos-
pheric ammonia:  Absorption by plant leaves.  Science 175:771-772.

Hutchinson,  G.   L.   1973.  Foliar absorption of atmospheric ammonia.
PH.D. Thesis, Univ. Illinois, Urbana.

Kincaid, D.  C., and N. P. Swanson.   1974.  Rainfall runoff from
irrigation furrows.  ASAE Trans.  17:266-268.
                                  113

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Linderman, C. L.  1973.  No mud like this since 1932.  Nebraska Farmer.
115:28.

Linderman, C. L., and N. P. Swanson.  1972.  Disposal of beef feedlot
runoff on corn.  Agron. Abstr., p. 182.

Linderman, C. L., N. P. Swanson, and L. N. Mielke. Riser intake designs
for feedlot solids collection basins.  (In review)

Lorimor, J. C.  1969.  Zeta potential studies of colloidal suspensions
from a beef cattle feedlot surface.  M.S. Thesis, University of Nebraska.

Lorimor, J. C., L. N. Mielke, L. F. Elliott, and J. R. Ellis.  1971.
Nitrate concentrations in groundwater beneath a beef cattle feedlot.
Paper #71-761.  ASAE, St. Joseph, Michigan.

Lorimor, J. C., L. N. Mielke, L. F. Elliott, and J. R. Ellis.  1972.
Nitrate concentrations in groundwater beneath a beef cattle feedlot.
Water Res. Bull. JJ:999-100S.

McCalla, T. M.  1972.  Pollution and waste management.  In:  The Earth
Around Us.  Soil Conservation Society of America, Ankeny, Iowa. p. 61-66.

McCalla, T. M.  1972.  Nebraska animal waste research.  In:  Proceedings,
Workshop on Livestock Waste Management, Ft. Collins, Colo.  Great Plains
Agr. Council Publ. 56:18-28.

McCalla, T. M.  1972.  Think of manure as a resource, not a waste.
Feedlot Management 12: 2 p.

McCalla, T. M.  1974.  Manure as a resource.  Nebraska Farm, Ranch and
Home Quarterly 21:4-6.                                              '

McCalla, T. M.  1973.  Use of animal wastes as a soil amendment.  Pro-
ceedings --Symposium on Utilization of Plant and Animal Byproducts,
Athens, Georgia [December, 1973).

McCalla, T. M.  1974.  Manure and runoff from feedlots.  ANCA Environ-
mental Sciences Committee Meeting, San Diego, California, January, 1974.
(In press)

McCalla, T. M., and L. F. Elliott.  1971.  The role of microorganisms in
the management of animal wastes on beef cattle feedlots.  In:  Livestock
Waste Management and Pollution Abatement, Amer.  Soc. Agr. Engineers,
St. Joseph, Michigan.p. 132-134.

McCalla, T. M., and L. F. Elliott.  1974.  Municipal and animal wastes
as fertilizers.  In:  1974 McGraw-Hill Yearbook on Science and Technol-
ogy.  McGraw-Hill Book Co., New York.p. 179-180.


                                  114

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McCalla, T. M.,  L.  F. Elliott, N. P. Swanson, and F. G. Viets, Jr.
1970.  Subsurface  cylindrical compartments for measuring chemical and
biological  conditions in  a beef cattle feedlot soil profile.  Agron.
Abstr., p.  110.

McCalla, T. M.,  J.  R. Ellis, and C. B. Gilbertson.  1972.  Chemical
studies of  solids,  runoff, soil profile and groundwater from beef
cattle feedlots  at  Mead, Nebraska.  In:  Waste Management Research.
Proc. 1972  Cornell  Agricultural Waste Management Conference, Syracuse,
N. Y.  p. 211-223.

McCalla, T. M.,  J.  R. Ellis, C. B. Gilbertson, and W. R. Woods.  1969.
Chemical studies of runoff following rainfall and snowmelt from beef
cattle feedlots.  Agron. Abstr., p. 84-85.

McCalla, T. M.,  J.  R. Ellis, and W. R. Woods.  1969.  Changes in the
chemical and biological properties of beef cattle manure during decom-
position,   Bact. Proc., p. 4-5.

McCalla, T. M.,  L.  R. Frederick, and G. L. Palmer.  1970.  Manure
decomposition  and fate of breakdown products in soil.  In:  Agricultural
Practices and Water Quality, T. L. Willrich and G. E. Smith, eds.
Iowa State  Univ. Press, Ames, Iowa, p. 241-255.

McCalla, T. M.,  and G. E. Schuman.  1972.   Pollution of air, soil and
water by livestock.  In:  Proceedings, Livestock Waste Management
Research Review, Lincoln, Nebraska (November, 1972).  p. 75-79.

McCalla, T. M.,  and G. E. Schuman.  1973.   How to guard.against pollu-
tion from beef cattle feedlot wastes.   In:  Livestock Waste Management
System Design Conference for Consulting and SCS  Engineers.   Lincoln,
Nebraska (February, lt)V3).  p.  Vil-1 to VII-9.

McCalla, T. M.,  and F. G. Viets, Jr.  1969.  Chemical and microbial
studies of wastes from beef cattle feedlots.   In:  Proceedings,
Pollution Research  Symposium, Lincoln, Nebraska,   p. 1-24.

Mielke, L.  N.  1973.  Encasing and undisturbed soil  cores in plastic.
Soil Sci. Soc. Amer. Proc. 37^:325-326.

Mielke, L.  N.  1973,  Nitrate in groundwater beneath a level feedlot.
In:  Proceedings, Nitrogen in Nebraska's  Environment Conference.
Lincoln, Nebraska (April, iy>^j.p. 157-173.

Mielke, L.  N.  1974.  Physical  characteristics of the surface and
interface layers of a level beef cattle feedlot.   Ph.D.  Thesis,
University of Nebraska, Lincoln.  Univ. Microfilms,  Ann Arbor, Mich.
                                  115

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Mielke, L. N., and J. R. Ellis.  1972.  Nebraska feedlot soil  coring
study.  I.  Scope and physical findings.  Agron. Abstr. p.  134.

Mielke, L. N., and J. R. Ellis.  1973.  Chemical and physical  charac-
teristics of soil profiles under abandoned feedlots.  Agron. Abstr.,
p. 126.

Mielke, L. N., and J. R. Ellis.  Nitrogen in soil cores and groundwater
under abandoned cattle feedlots.  J. Environ. Qual.  (In review)

Mielke, L. N., J. R. Ellis, N. P. Swanson, J. C. Lorimor, and  T. M.
McCalla.  1970.  Groundwater quality and fluctuation in a shallow un-
confined aquifer under a level feedlot. In:  Relationship of Agriculture
to Soil and Water Pollution.  Proceedings, Cornell Univ. Conference on
Agricultural Waste Management, Rochester, N. Y.  p. 31-40.

Mielke, L. N.  N. P. Swanson, and J. C. Lorimor.  1969.  Some  physical
characteristics of beef cattle feedlots.  Agron. Abstr., p. 85.

Mielke, L. N., N. P. Swanson, and T. M. McCalla.  1971.  Soil  profile
conditions affected by beef cattle feedlots.  EOS, Trans. AGU  52:827.

Mielke, L. N.,N. P. Swanson, and T. M. McCalla.  1974.  Soil profile
conditions of cattle feedlots.  J. Environ. Qual. 3:14-17.

Mosier, A. R.  1973.  Inhibition of Chlorella ellipsoidea population
growth by aliphatic amines.  Agron. Abstr., p. 179.

Mosier, A. R.  1974.  Effect of cattle feedlot volatiles, aliphatic
amines, on Chlorella ellipsoidea growth.  J. Environ. Qual. 3^:26-28.

Mosier, A. R.  1974.  Effect of aliphatic amines on Chlorella.  Ph.D.
Thesis, Colorado State Univ., Ft. Collins.

Mosier, A. R.  1974.  Effect of aliphatic amines on Chlorella  ellip-
soidea nitrogen uptake, photosynthesis, and respiration,  J. _A_g_r_.__Fp_o_d
Chem.  (In review)

Mosier, A. R.  1974.  The fate of aliphatic amines in a fresh  water
ecosystem.  J. Environ. Qual. (In review)

Mosier, A. R., and C. E. Andre.  1973.  Direct gas chromatographic
analysis of aqueous solutions of aliphatic N-nitrosamines.  Analyt.
Chem. 45:372-575.

Mosier, A. R., C. E. Andre, and F. G. Viets, Jr.  1973.  Identification
of aliphatic amines volatilized from a cattle feedyard.  Environ. Sci.
Techno1. 7:642-644.
                                  116

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Hosier, A. R., K. Haider, and F. E. Clark.  1972.  Water-soluble
organic substances leachable from feedlot manure.  J. Environ. Qual.
1:320-323.

Nienaber, J. A., C. B. Gilbertson, T. M. McCalla, and F. M. Kestner.
1974.  Disposal of effluent from a beef cattle feedlot runoff-control
holding pond.  ASAE Trans ]7;575-378.

Norstadt, F. A.  1971.  Nutrients from animal wastes.  In:  Pollution
Abatement Through Soils and Water Management.  Proceedings of Workshop,
Portland, Oregon, USDA Soil Conservation Service, p. 29-51.

Norstadt, F. A.  1971.  The relation of animal wastes to land use
management.  In:  Pollution Abatement Through Soils and Water Manage-
ment.  Proceedings of Workshop, Portland, Oregon, USDA Soil Conservation
Service,  p. 83-97.

Norstadt, F. A.  1972.  Problems and status of research in the plains.
Minutes of Discussion of Afternoon Session, March 12.  In:  Proceedings
of Workshop on Livestock Waste Management (Fort Collins, Colo.).Great
Plains Agr. Council Pub. 56.

Norstadt, F. A.  1973.  Effects of a beef cattle feedlot on underlying
soil.  (Abstr.)  Proceedings Colorado State Univ. Annual Exp. Station
Conference.

Norstadt, F. A., and H. R. Duke.  1974.  Beef cattle feedlots:  Impact
on underlying soil.  (Abstr.)  Proceedings Colorado State Univ. Annual
Exp. Sta. Conference.

Norstadt, F. A., and H. R. Duke.  1974.  Feedlot no pollution threat
to soil and water.  Colorado State Univ.  AgriSearch 1(7):1-2.

Peterson, J. R., T. M. MCalla, and G. E. Smith.  1971.  Human and
animal wastes as fertilizers.  In:  Fertilizer Technology and Use.
2nd ed.  Soil Sci. Soc. America, Madison, Wis., p. 557-596.

Porter  L. K.  F. G. Viets, and G. L, Hutchinson.  1972.  Air contain-
ing nitrogen-15 ammonia:  Foliar absorption by corn seedlings.  Science
175:759-761.

Schnieder, R. D., J. A. DeShazer, and L. F. Elliott.  Save your breath!
1974 Nebraska Swine Report.  E. C. 74-219:19-20

Schuman, G. E. 1974.  Animal wastes:  Phytotoxic effects on plant
growth; influence on the feedlot soil profile.  Ph.D. Thesis, Univ.
of Nebraska, Lincoln.
                                  11-7

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Schuman, G. E,, and T. M. McCalla.  Chemical characteristics of a
feedlot soil profile.  Soil Science (In press) .

Schuman, G. E., M. A. Stanley, and D.  Knudsen.   1973.  Automated total
nitrogen analysis of soil and plant samples.  Soil Sci. Soc. Amer.
Proc.
Stewart, B. A.  1970.  Volatilization and nitrification of nitrogen
under simulated feedlot conditions.  J. Environ. Sci. § Technol.
£: 579-582.

Sukovaty, J. E.  1973.  Some effects of beef feedlot effluent applied
to forage sorghum.  M.S. Thesis, University of Nebraska, Lincoln.

Sukovaty, J. E., L. F. Elliott, and N. P. Swanson.  1973.  Effects of
feedlot runoff on soil and forage sorghum.  Agron. Abstr. , p. 183.

Sukovaty, J. E., L. F. Elliott, and N. P. Swanson.  1974.  Some effects
of beef-feedlot effluent applied to a forage sorghum grown on a Colo
silty clay loam soil.  J. Environ. Qual. 3{4) : 381-388.

Swanson, N. P.  1972.  Research needs for the design and management of
beef feedlot runoff control systems.  In:  Proceedings, Livestock Waste
Management Research Review, Lincoln, Nebraska~~(TulyY 1972J .   Great
Plains Agr. Council Publ. No. 60.

Swanson, N. P.  1973.  Hydraulic considerations for design.   In:
Proceedings, Livestock Waste Management System Design Conference for
Consulting and SCS Engineers, Lincoln, Nebraska (February, 1973) .
p. III-l to 111-18.

Swanson, N. P.  1973.  Typical and unique waste disposal systems.  In:
Proceedings, Livestock Waste Management System Design Conference for
Consulting and SCS Engineers/ Lincoln^ Nebraska (February, 1973) .
p. XII-A1 to XII-A2, and XIII-B1 to XIII-B3.

Swanson, N. P.  1973.  A programmed sampler for runoff and bedloads.
ASAE Trans. 16_: 790-792.

Swanson, N. P., and C. B. Gilbertson.  1974.  Sampling liquid and non-
fluid wastes.  Proc., SEC-412 Animal Waste Conference, ASAE  (In press).

Swanson, N. P., arid L. Jackson.  1973.  Management and maintenance
design considerations.  In:  Proceedings, Livestock Waste Management
System Design Conference for Consulting and SCS Engineers, p. XII-01 to
XI I -06.  Lincoln, Nebraska (February, 1973).
                                  118

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 Swanson, N.  P., C.  L.  Linderman, and J.  R.  Ellis.   1974.   Irrigation
 of perennial forage crops with feedlot runoff.   ASAE Trans.  17:144-147.

 Swanson, N.  P., and C.  L. Linderman.   1974.   Low-cost disposal systems
 for feedlot  runoff.  Mid-central ASAE Meeting,  St.  Joseph,  Missouri
 (April 1974).   Agr. Engr. _55_: 20-21.

 Swanson, N.  P., J.  C.  Lorimor, and L.  N.  Mielke.   1973.   Broad-basin
 terraces for sloping cattle feedlots.  ASAE  Trans.  16;746-749.

 Swanson, N.  P., and L.  N. Mielke.   1973.  Solids trap for beef cattle
 feedlot  runoff.  ASAE  Trans.  16_:743-745.

 Swanson, N.  P., L.  N.  Mielke,  and J.  C.  Lorimor.   1970.   Hydrologic
 studies  for  evaluation  of the  pollution  potential  of feedlots  in
 eastern  Nebraska.   In:   Relationship  of  Agriculture  to Soil  and Water
 Pollution.   Proceedings,  Cornell Univ. Conference  on Agricultural Waste
 Management,  Rochester,  N.  Y.   (January,  1970).  p.  226-232.

 Swanson, N.  P., L.  N. Mielke,  J.  C. Lorimor, T. M. McCalla,  and J. R.
 Ellis.   1971.   Transport  of pollutants from  sloping  cattle feedlots  as
 affected by  rainfall intensity,  duration, and recurrence.  In:  Live-
 stock  Waste  Management  and Pollution Abatement.  Amer. Soc.  Agr.
 Engineers, St.  Joseph,  Michigan.p. 51-55.

 Swanson,  N.  P.,  L.  N. Mielke,  J. C. Lorimor, T. M. McCalla,  and
 J.  R.  Ellis.  1971.  Effect of rainfall intensity, duration, and
 recurrence on the transport of pollutants from sloping cattle  feedlots.
 (Abstract).  International Symposium on Livestock Wastes, Columbus,
 Ohio.  p. 15.

 Viets, Frank G., Jr.  1970.  The pollution potential of cattle  feeding
 operations.  In:  Proceedings  of Symposium on Agriculturally Related
 Pollution and Fertilizer  Conference.  Bozeman, Montana,  p.  11-16.

 Viets, F. G., Jr.   1971.  The mounting problem of cattle feedlot pollu-
 tion.  Agr. Sci. Rev. 9:1-9.

Viets, F. G., Jr.   1971.  Cattle feedlot pollution.  In:  Proceedings
National Symposium  on Animal Wastes, Airlie House,  Warrenton, Virginia.
Washington, D.  C. Council of State Governments,   p, 97-105.

Viets, F. G., Jr.   1974.  Animal wastes and fertilizers as potential
sources of nitrate pollution of water.  Proc. FAO/IAEA Panel on Isoto-
pic Tracer-aided Studies on the Fate and Significance of Agrichemical
Residues with Particular Reference to Nitrates.   Presented in Vienna
 (June, 1973).   (In press) .
                                  119

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Viets, F. G., Jr.  1974.  The fate of nitrogen in the environment under
intensive animal feeding.  Federation Proc. 33:1178-1182.

Woods, W., T. M. McCalla, C. B. Gilbertson and J. R. Ellis.  1972.
Waste management and animal performance in beef feedlots.  1972 Beef
Cattle Report.  Nebraska Agr. Exp. Sta. EC 72-218: 26-28.
                                 120

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 [I III I'OH I NO.
 | EPA-660/2-75-015
                                    TECHNICAL REPORT DATA
                                           ts on ilic reverse before completing)
  •i. n n.L AND sun n rut
  POLLUTION ABATEMENT FROM CATTLE FEEDLOTS  IN
  NORTHEASTERN COLORADO AND NEBRASKA
/.AUTHORIAL. K> Porter, F.  G.  Viets,  Jr., T. M. McCalla,
   F.  Elliott, F. A. Norstadt,  H.  R.  Duke, N. P. Swanson,
J--. N.  Mieike. G. L. Hutchinson.  A.  R.  Mosier. and G. E. s
H. r-tRt-oHMiNo OHO •VNIZATION NAME AND ADDRESS
        AGRICULTURAL  RESEARCH SERVICE
        UNITED STATES DEPARTMENT OF AGRICULTURE
        P. 0. Box E
        Fort Collins,  Colorado 80521	
  I/. SPONSORING AGENCY NAME AND ADDRESS
        INTERAGENCY AGREE.MENT BETWEEN
        U.  S. Department  of Agriculture and
        Environmental Protection Agency
                                                           3. RECIPIENT'S ACCESSiOM-NO.
                                                           5. REPORT DATE
                                                             July 1974
                                                           6. PERFORMING ORGANIZATION CODE
                                                            8. PERFORMING ORGANIZATION REPORT NO.
                                                            10. PROGRAM ELEMENT NO.
                                                           11. CONTRACT/GRANT NO."
                                                            EPA-IAG  -04-044*
                                                           13. TYPE OF REPORT AND PERIOD COVERED
                                                           14. SPONSORING AGENCY CODE
  1C, SUPPLEMENTARY NOTES
   ;ABSTRACT climatic factors, feedlot  runoff,  and organic material  in  the runoff were	
 evaluated in experimental and  commercial feedlots.  The effects of Slope,  stocking
 rates,  terraces, basins, and holding ponds were evaluated to obtain  the best controls
 for  containing runoff.  In eastern Nebraska,  70 cm annual precipitation produces 23 cm
 of runoff;  whereas, in northeastern  Colorado,  37 on annual precipitation gives only 5 5
 cm of runoff.   Large applications of runoff liquid, up to 91 cm on grass-Ladino and 76
 cm on corn,  in Nebraska did not decrease yields; however, in northeastern  Colorado, the
 concentrated high-salt runoff required  dilution before direct application  to crops!  Th
 organic manure-soil interface severely  restricts the movement of water,  nitrates,
 organic substances, and air into the soil beneath feedlots.   The amounts of  N03-N  in
 soil cores  taken from Nebraska feedlots  and croplands ranked as follows:   abandoned
 feedlots  >  feedlot  cropland > upland feedlots  > river valley feedlots > manure mounds >
 alfalfa > grassland.   Feedlots contribute  NH3,  amines,  carbonyl sulfide, H2S,  and  other
 unidentified substances to the atmosphere.  Ammonia and amine can be scavenged from the
 air by green plants and water bodies.  Anaerobic conditions  in feedlots are  conducive
 to the production of carbonyl sulfide, H2S, and amines.   Management practices,  such as
 good drainage,  that enhance aeration will  decrease the  evolution of these  compounds.
                                KEY WORDS AND DOCUMENT ANALYSIS
                  DESCRIPTORS
Agricultural wastes
Cattle
Livestock
Waste disposal
                                             b.lDENTIFIERS/OPEN ENDED TERMS
                                             Rainfall  runoff
                                             Animal wastes
                                             Feedlots
                                             Land application
                                             Water pollution potential
                                             Wastes characteristics
                                                                         c.  COSATI Field/Group
                                                                         02/03
                                                                         02/04
                                                                         02/05
          STATEMENT

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