<title>Risk Assessment Evaluation for Concentrated Animal Feeding Operations</title>
<type>single page tiff</type>
<keyword>manure animal soil water waste composting swine application wetlands pathogens nitrogen land cafos systems cafo poultry management anaerobic organic runoff</keyword>
<author> United States. Environmental Protection Agency. Office of Research and Development. ; National Risk Management Research Laboratory (U.S.).</author>
<publisher>U.S. Environmental Protection Agency, Office of Research and development, National Risk Management Research Laboratory,</publisher>
<subject> Environmental risk assessment--United States ; Effluent quality ; Animal waste ; Manures ; Livestock--Manure--Environmental aspects ; Feedlots ; Nutrient pollution of water</subject>
Evaluation for Concentrated
Animal Feeding Operations
Risk Management Evaluation For
Concentrated Animal Feeding Operations
U.S. Environmental Protection Agency
Office of Research and Development
National Risk Management Research Laboratory
[This Page Intentionally Left Blank]
The U.S. Environmental Protection Agency (EPA) is charged by Congress with protecting the Nation's
land, air, and water resources. Under a mandate of national environmental laws, the Agency strives to
formulate and implement actions leading to a compatible balance between human activities and the ability
of natural systems to support and nurture life. To meet this mandate, EPA's research program is providing
data and technical support for solving environmental problems today and building a science knowledge base
necessary to manage our ecological resources wisely, understand how pollutants affect our health, and
prevent or reduce environmental risks in the future.
The National Risk Management Research Laboratory (NRMRL) is the Agency's center for investigation of
technological and management approaches for preventing and reducing risks from pollution that threaten
human health and the environment. The focus of the Laboratory's research program is on methods and their
cost-effectiveness for prevention and control of pollution to air, land, water, and subsurface resources;
protection of water quality in public water systems; remediation of contaminated sites, sediments and
ground water; prevention and control of indoor air pollution; and restoration of ecosystems. NRMRL
collaborates with both public and private sector partners to foster technologies that reduce the cost of
compliance and to anticipate emerging problems. NRMRL's research provides solutions to environmental
problems by: developing and promoting technologies that protect and improve the environment; advancing
scientific and engineering information to support regulatory and policy decisions; and providing the
technical support and information transfer to ensure implementation of environmental regulations and
strategies at the national, state, and community levels.
This publication has been produced as part of the Laboratory's strategic long-term research plan. It is
published and made available by EPA's Office of Research and Development to assist the user community
and to link researchers with their clients.
Lawrence W. Reiter, Acting Director.
National Risk Management Research Laboratory
The National Risk Management Research Laboratory (NRMRL) developed a Risk Management Evaluation
(RME) to provide information to help plan research dealing with the environmental impact of concentrated
animal feeding operations (CAFOs). Methods of animal production in the U.S. have undergone fundamental
changes in the last 30 years. The majority of meat, dairy, and poultry production has been concentrated into
large facilities. Dairies with more than 2,000 cows and swine operations with more than 10,000 hogs are not
unusual. Broiler houses with 50,000 birds are common. With the concentration of animals has come a
concomitant concentration of manure production. One animal facility with a large population of animals can
easily equal a small city in terms of waste production. Current practices of waste handling often include
minimal or no treatment before the wastes are disseminated into the environment. The RME was developed
to provide characterization of the waste problem, and a description of common environmental stressors and
their movement including the air transport of pollutants. Current risk management practices in the animal
industry are described, along with treatment approaches such as anaerobic/aerobic digestion, constructed
wetlands, and disturbed land reclamation. Finally, suggested areas for future research are presented to help
focus planning for the near future.
Table of Contents
1 OVERVIEW OF RISK MANAGEMENT DOCUMENT 1
2 INTRODUCTION 6
2.1 Agricultural Sectors Considered in this Document 6
3 MANURE PRODUCTION AND MANAGEMENT 7
3.1 Manure Quantities Among Animal Populations 7
3.1.1 Poultry 9
184.108.40.206 Broilers/Roasters and Turkeys 10
220.127.116.11 Layers 11
3.1.2 Swine 12
3.1.3 Cattle 15
18.104.22.168 BeefFeedlots 15
22.214.171.124 Dairy 17
3.2 Manure Characteristics 19
3.2.1 Physical Properties 20
3.2.2 Nutrient Content and Form from Poultry 21
126.96.36.199 Layers, Broilers, and Turkeys 21
188.8.131.52 Layers 21
184.108.40.206 Nutrient Content and Form from Swine 21
220.127.116.11 Nutrient Content and Form from Cattle 21
3.3 Manure Management Practices 22
3.3.1 Wet Manure Management 22
3.3.2 Dry Manure Management 22
4 WATERSHED STRESSORS IN CAFO WASTE 24
4.1 Nutrients 24
4.1.1 Nitrogen 25
4.1.2 Phosphorus 27
4.1.3 Mineral Salts 28
4.2 Pathogens 28
4.2.1 Pathogens of Concern at CAFOs 29
18.104.22.168 Bacteria 29
22.214.171.124 Fungi 30
126.96.36.199 Viruses 30
188.8.131.52 Helminths 30
184.108.40.206 Protozoa 30
4.2.2 Disease Descriptions 31
4.2.3 Effects of Pathogen Pollution 32
4.2.4 Human Diseases: Examples of Manure-Related Human Epidemics, Case Studies of
Problems and Potential for Problems with Pathogens in Animal Manure 33
220.127.116.11 Walkerton, Ontario 33
18.104.22.168 Washington County Fair, New York 33
22.214.171.124 Carrolton, GA 34
126.96.36.199 Wilshire, Swindon, and Oxfordshire, England 34
188.8.131.52 Bradford, England 34
184.108.40.206 Milwaukee, Wisconsin 34
220.127.116.11 Maine 34
18.104.22.168 Sakai City, Japan 34
22.214.171.124 Cabool, Missouri 34
4.2.5 Animal Diseases 35
4.3 Antibiotics 36
4.3.1 Case studies on the effect of antibiotics related to CAFOs on the environment: 37
126.96.36.199 Case 1 - Chesapeake Bay 37
188.8.131.52 Case 2 -Iowa Swine Operations 37
184.108.40.206 Case 3 - Shoal Creek 38
220.127.116.11 Case 4 -A National Reconnaissance 38
4.4 Endocrine Disrupting Chemicals Associated with Concentrated Animal Feeding Operations....38
4.4.1 Xenobiotic Hormones 40
4.4.2 Uses of Hormones in CAFOs 41
4.4.3 Release of Hormones to the Environment 42
4.5 Metals 43
4.5.1 Use of Metals in Animal Feed 43
4.5.2 Mobility of metals in soil 43
4.5.3 Metals in plants 45
4.5.4 Metals in Animals 46
4.5.5 Summary 46
5 STRESSOR TRANSPORT 48
5.1 Transport Mechanisms 48
5.1.1 Overland Transport in Wet Weather Flow 48
5.1.2 Physical and Chemical Processes Affecting Sediment Impacts 48
5.1.3 Overland Flow 48
5.1.4 Interflow 49
5.1.5 Groundwater flow 49
5.2 How These Processes Impact Typical CAFO Operations 49
5.2.1 Suspended Solids and Sediments (SSAS) 50
5.2.2 Stress due to SSAS 51
5.3 Groundwater Transport 52
5.3.1 Statement of Problem 52
5.3.2 Pollutants, Sources, Transport, and Fate 53
18.104.22.168 Nitrogen 53
22.214.171.124 Ammonia 53
126.96.36.199 Nitrate 54
188.8.131.52 Phosphorus 55
184.108.40.206 Pathogens 56
5.3.3 Risk Management 57
5.3.4 Storage Facilities 57
5.3.5 Farming Practices 58
5.3.6 Natural Filters 61
6 AIR TRANSPORT AND DEPOSITION 63
6.1 Current Air Quality Issues Associated with Agriculture 63
6.1.1 Ammonia 63
6.1.2 Nitrous Oxide 64
6.1.3 Methane 64
6.1.4 Carbon dioxide 65
6.1.5 Hydrogen sulfide 65
6.1.6 Criteria Air Pollutants 65
6.2 Generation of Air Emissions Resulting from Operational Variables 66
6.2.1 Air Emissions from Land Application Activities 66
6.2.2 Odors 68
6.2.3 Paniculate Matter 68
6.3 SUMMARY 69
7 RISK MANAGEMENT OPTIONS FOR CAFO WASTE 70
7.1 Land Application 70
7.2 Practices Used in Land Application 71
7.2.1 Application Systems 71
7.2.2 Potential Problems Associated with Manure Applications 72
7.2.3 Soil Management Practices to Reduce Problems 74
7.2.4 Runoff Control from Land Application Fields 74
220.127.116.11 Reducing Soil Detachment 74
18.104.22.168 Reducing SSAS Transport within a Field 75
22.214.171.124 Trapping Sediment after the Field 75
7.3 Composting of CAFO wastes 77
7.3.1 What is Composting? 77
7.3.2 Composting systems 78
126.96.36.199 Interventionary Systems 78
188.8.131.52 Non-Interventionary Systems 78
7.3.3 Comparison of Interventionary and Non-interventionary Systems 78
7.3.4 Composting in the Beef and Dairy Industries 78
184.108.40.206 Beef 78
220.127.116.11 Dairy 79
18.104.22.168 Composting Swine Waste 79
22.214.171.124 Composting Poultry Waste 80
7.3.5 Composting Concerns and Problems 81
126.96.36.199 Nutrients 81
188.8.131.52 Pathogens 81
7.3.6 Land Application of Compost 83
7.4 A Strategy Requiring Some Additional Research-Anaerobic Digestion 83
7.4.1 Technology Description 83
184.108.40.206 Covered Lagoons 83
220.127.116.11 Complete Mix Digester 84
18.104.22.168 Plug-flow Digester 85
7.4.2 Application 85
7.4.3 Operation and Performance 86
7.4.4 Fuel Gas Production 87
7.5 Technologies Requiring Significant Additional Research Before Implementation-Aerobic
Digestion-Wetlands-Land Reclamation 88
7.5.1 Aerobic Digestion 88
22.214.171.124 Types of Aerobic Digest!on Technologies 89
126.96.36.199 Application 89
7.5.2 Wetlands 90
188.8.131.52 Constructed Wetlands 90
184.108.40.206 Restored Wetlands 90
220.127.116.11 Enhancement Wetlands 90
18.104.22.168 Free Water Surface (FWS) Wetlands 90
22.214.171.124 Vegetated Submerged Bed (VSB) Wetlands 91
126.96.36.199 Reciprocating (ReCip) wetlands and vertical-flow (VF) wetlands 91
7.5.3 Treatment Mechanisms 91
7.5.4 Plant Functions 92
7.5.5 Risk Associated with Constructed Wetlands 93
7.5.6 Application and Performance of Constructed Wetlands for Agricultural Wastewaters 94
7.5.7 Processes to Significantly Reduce Pathogens (PSRP) 97
7.5.8 Recommendation 97
188.8.131.52 Composting 97
184.108.40.206 Air Drying 98
220.127.116.11 Facultative lagoons / Storage 98
18.104.22.168 Anaerobic Digestion 98
22.214.171.124 Aerobic Digestion 99
126.96.36.199 Lime Stabilization 99
7.6 Land reclamation 100
7.6.1 Non-Farm Land Applications 100
7.6.2 Phytoremediation Projects, Sediment Recycling, and Landfill Covers 100
7.6.3 Riparian Corridors 100
7.6.4 Forest Products: Short Rotation Wood Crops-Pulp & Paper, Lumber, Fuel 100
7.6.5 Highways: Roadsides and Medians 101
8 RESEARCH NEEDS ASSOCIATED WITH CAFOS 102
8.1 Overview 102
8.2 Stressor Evaluation and Quantification 102
8.3 Process Research 103
8.4 Fate and Effects of Stressors in the Environment 103
8.5 Ground Water 104
8.6 Aerosol Research 105
8.7 Land Reclamation 106
9 REFERENCES 107
List of Tables
Table 3.1 Change in Animal Units, 1982 to 1997 7
Table 3.2 Change in CAFO Operations from 1982 to 1997 8
Table 3.3 Manure Production per 1000 Pounds Live Weight on an Annual Basis 9
Table 3.4 Nitrogen and Phosphorus Content of Animal Waste 20
Table 3.5 Characteristics of Animal Manure Based on 1000 Pound Live Weight 20
Table 4.1 Diseases and Animals Commonly Identified as Sources of the Causative Organisms 30
Table 4.2 Examples of Manure-Related Human Epidemics 33
Table 4.3 Sources of Common Zoonotic Diseases on Farms 36
Table 4.4 Antibiotic Levels in the Lagoons and in One Monitoring Well (adapted from Table 7)
(Iowa Dept. Public Health, 1997) 37
Table 4.5 Hormones Approved for Veterinary Use in Cattle 42
Table 4.6 Copper and Zinc in Swine Diets 43
Table 4.7 Soil Cu Balance after Five Years of Repeated Pig Slurry Application 44
Table 4.8 Soil Zn Balance after Five Years of Repeated Pig Slurry Application 44
Table 4.9 Cu and Zn in Soil (top 5 cm) February, 1987 and Herbage First Cut of 1986 45
Table 7.1 Functions of Soil Conservation Practices (adapted from USEPA, 2001a) 76
Table 7.2 Status of Farm-Based Digesters in the United States 85
Table 7.3. Performance Data Summarized for Gulf of Mexico Program (CH2M-Hill,1997) 94
Table 7.4. Agricultural Treatment Wetlands intheNADB 94
Table 7.5. Range of Costs and Operating Parameters for NADB Agricultural Treatment Wetlands 95
Table 7.6. 95% Confidence Interval about the Mean for all NADB Agricultural Treatment Wetlands ..95
Table 7.7. Preliminary Averages for ReCip System Treating Swine Wastewater 97
Table 7.8. Microbiological Quality Guidelines and Standards for Application of Wastes to Land 98
Table 7.9. Effects of Waste Treatment and Management Systems on Pathogen Reduction 99
List of Figures
1.1 Phosphorus Assimilative Capacity for Farms 2
1.2 Excess Phosphorus on Farms with No Export 3
3.1 Poultry Production distribution in the United States 10
3.2 Turkey Production Distribution in the United States 11
3.3 Layer and Pullet Distribution in the United States 12
3.4 Change in Swine Production Distribution in the United States 13
3.5 Swine confinement barns with lagoon 14
3.6 Swine pens inside barn with slatted floors 14
3.7 Change in Cattle Locations as of the 1997 Census 15
3.8 Aerial view of afeedlot in Kansas with a lagoon 16
3.9 Change in Distribution of Dairy Cattle in the United States 17
3.10 Dairy farm with a manure storage tank 18
3.11 Dairy farm with poor manure management and detrimental impact on the environment 19
4.1 Depiction of Carbon and Nitrogen Cycles in Soils or Sediments 26
4.2 Diagrammatic Illustration of Preferential Flow through Macropores and Interstitial (porewater)
Flow in the Soil Matrix 27
4.3 Frequency of Detection of Organic Wastewater Contaminants by General Use Category (4A), and
Percent of Total Measured Concentration of Organic Wastewater Contaminants by General Use
Category shown above Bar (Kolpin, et al., 2001) 39
4.4 Structure of Biogenic Hormones 40
4.5 Chemical Structure of Trenbelone Acetate and Hydroxide 41
5.1 Transport Pathways of Pollutants Derived from Animal Waste 54
5.2 Nitrogen-Carbon Cycling in Soil/Sediment Derived from Animal Waste 55
5.3 Diagrammatic Illustration of Preferential Flow through Macropores and Interstitial (Pore-Water)
Flow in the Soil Matrix 56
5.4 Concrete manure storage tank. Structures of this type will prevent leakage of wastes into groundwater.... 59
5.5 A new lagoon with a synthetic geotextile liner to prevent seepage into groundwater 60
5.6 Terraced fields to prevent erosion of soil on sloping land 61
6.1 High velocity sprinkler, a potential source of airborne contaminants 67
6.2 Tank truck applying manure with the potential for aerosol generation 67
7.1 Tractor drawn liquid manure application after corn harvest 72
7.2 Means of Manure Disposal by Animal Sector 72
7.3 Mixed compost from turkey waste 80
7.4 Turkey waste compost with wood chips and feathers 81
7.5 Truck mounted spreader applying compost to afield 84
7.6 Covered manure tank generating methane in Iowa 86
7.7 Free Water Surface (FWS) Wetlands 91
7.8 Vegetated Submerged Bed (VSB) Wetland 92
7.9 View of a hog operation with a lagoon flowing into constructed wetlands for treatment of wastewater 96
7.10 Ground level view of constructed wetland with the owner making observations for his records 96
The editors wish to thank S. Stoll for detailed assistance in editing this document for editorial quality.
In addition, several figures were derived from the USDA National Resources Conservation Service website
and included in this document. The NRCS website is also a source for the pictures used in this document.
The NRCS Photo Gallery contains natural resource and conservation related photos from across the USA.
The Gallery is a joint project between NRCS Conservation Communications and the NRCS Information
Technology Center in Ft. Collins, Colorado.
Photos in the Gallery are available free of charge in two common image formats: TIFF or JPEG. Image
resolution is generally 1500 x 2100 pixels (5" x 7" at 300 dpi). TIFF images are 32 bit CMYK color,
ranging from 6 mb to 12 mb in size. JPEG images are 24 bit RGB color ranging from 200 kb to 400 kb in
If you use any of these photos in a publication, on a web site, or as part of any other project, please use one
of the following credit lines:
• Photo by (photographer's name), USDA Natural Resources Conservation Service.
• Photo courtesy of USDA Natural Resources Conservation Service.
• Photo courtesy of USDA NRCS.
These photos may not be used to infer or imply NRCS endorsement of any product, company, or position.
Please do not distort or alter the images the photos portray.
Other figures were derived from the USDA National Agricultural Statistics Service website and included in
The list of figures derived from the NRCS and NASS is as follows:
Cover photographs NRCS
Figure 1.1 NRCS
Figure 1.2 NRCS
Figure 3.1 NRCS
Figure 3.2 NASS
Figure 3.3 NASS
Figure 3.4 NRCS
Figure 3.9 NRCS
Photographs as Figures
Figure 3.5 NRCS
Figure 3.6 NRCS
Figure 3.8 NRCS
Figure 3.10 NRCS
Figure 3.11 NRCS
Figure 5.4 NRCS
Figure 5.5 NRCS
Figure 5.6 NRCS
Figure 6.1 NRCS
Figure 6.2 NRCS
Figure 7.1 NRCS
Figure 7.3 NRCS
Figure 7.4 NRCS
Figure 7.5 NRCS
Figure 7.6 NRCS
Figure 7.9 NRCS
Figure 7.10 NRCS
Edwin Barth Aerosols
Dr. Donald Brown Wetlands
Dr. John Cicmanec Pathogenic Organisms and Background
Jennifer Goetz Antibiotics
Dr. John Haines Land Application
Dr. Mohamed Hantush Groundwater
Ronald Herrmann Composting
Dr. Paul McCauley Nutrients
Kim McClellan Aerosols
Dr. Marc Mills Sediments and Wet Weather Flow
Teri Richardson Digestion
Steven Rock Land Reclamation
Sally Stoll Metals
Dr. Gregory Sayles Endocrine Disrupting Compounds
Dr. James Smith Pathogenic Organisms
Stephen Wright Sediments and Wet Weather Flow
Editors: Dr. John Haines and Laurel Staley
1 OVERVIEW OF RISK MANAGEMENT DOCUMENT
This document is intended to help the reader gain an understanding of potential environmental
problems associated with Concentrated Animal Feeding Operations (CAFOs). Although a variety of
animals are raised in CAFOs, this document will focus on beef, dairy, swine and poultry. The quantities and
characteristics of manure produced by the different animals are presented. The watershed stressors resulting
from CAFO pollution are discussed, as are the transport mechanisms that disperse them through the
environment. Common manure management practices are also presented.
Because large numbers of animals are confined in relatively small areas at CAFOs, a very large
volume of manure is produced and must be kept in a correspondingly small area until disposed of. The age-
old practice of land application is used, but the volumes of manure that must be disposed in this way
frequently exceed the assimilative capacity of land within economic transport distances. This may result in
the release of excess manure to watershed environments during the catastrophic breach of holding facilities
or more commonly, during the intermittent runoff of excess manure applied to already saturated land.
Figure 1.1 shows the phosphorus assimilative capacity of farmland in the United States. Figure 1.2 shows
the excess phosphorus available on farms with no export. Clearly, an imbalance exists between available
phosphorus and the capacity of the land to absorb phosphorus. The same general relationship holds for
nitrogen. If land in entire counties were available for application of animal waste, the overburden of
nutrients is somewhat relieved, but excess quantities of nutrients still exist in some locales. Neither of the
maps shown takes into account fertilizer applied to fields.
This would be a problem even if manure contained only beneficial nutrients. In excess amounts,
these nutrients damage, not improve, soil fertility and may pollute nearby water. More importantly,
however, manure from CAFOs contains components other than nutrients. The dominant element in manure
is carbon. Many of the carbon compounds in manure may contribute to oxygen depletion in water. The
nutrient elements N and P in manures may also contribute to eutrophication of water if their entry into water
is not controlled. Modern agriculture with its emphasis on intensive housing and speeding the growth of
livestock to market weight has employed a variety of substances that have not been used before in animal
husbandry. These include antibiotics to combat the spread of disease among animals housed in close
quarters, natural and synthetic hormones to speed growth, and metals (As, Cu, Zn) to do the same and
preserve the freshness of feed. When present in the large amounts of manure generated at CAFOs and
stored on-site, these other substances pose a threat to the environment. The effects of antibiotics on native
soil bacteria are largely unknown. The effects of biogenic and synthetic hormones on other animals and
humans are largely unknown.
Capacity Of Cropland And Pastureland
To Assimilate Manure Phosphorus, 1997
Figure 1.1. Phosphorus assimilative capacity for farms.
This Risk Management Evaluation (RME) is intended to document the salient environmental risks
associated with hog, poultry, dairy and beef CAFOs and actions that could be taken to reduce those risks
now. Areas in which further research is needed are identified and discussed in Section 8 of this document.
In reviewing the existing body of knowledge on intensive livestock agriculture, the following points
• Underlying all of the environmental problems associated with CAFOs is the fact that too much
manure accumulates in restricted areas. Traditional means of using manure are not adequate to
contend with the large volumes present at CAFOs.
• The nutrient load from CAFOs is large, with about 2.5 billion pounds of N and 1.4 billion pounds of
P recoverable in manure. Total manure N is about 12.9 billion pounds and total manure P is about
3.8 billion pounds.
Excess Manure Phosphorus
Assuming No Export Of Manure From Farm, 1997
Figure 1.2. Excess phosphorus on farms with no export.
• CAFO manure contains potentially pathogenic microorganisms. The combination of large herds and
closely confined housing makes it likely that at least some animals are asymptomatic carriers of
pathogenic organisms. Once introduced, these pathogens may readily spread among the closely
confined herd. Shed into the manure, these pathogens find favorable breeding grounds in the barns,
manure storage and handling systems and are released into the watershed environment routinely
during the land application of waste.
• The antibiotics administered to CAFO livestock may contribute to the development of antibiotic
resistant strains of pathogens - especially those harbored within the livestock raised at these
facilities. The sub-therapeutic use of antibiotics at CAFOs aggravates the problem.
• Naturally occurring and synthetic hormones administered to livestock to speed growth to market
weight pollute the environment when released along with manure during land application or during
an accidental release. The environmental effects of these compounds are largely unknown.
• Metals used as feed supplements to promote livestock growth may degrade the quality of the land to
which waste is applied. Adverse environmental effects may result when waste containing metals is
released into the watershed.
• Transport pathways for stressors from CAFOs encompass surface runoff, air transport and
redeposition, and groundwater flow. Nutrients, pathogenic organisms, hormones and metals may
easily reach waterbodies via these means.
There are measures that may be taken now to mitigate the risk posed by the large volumes of manure at
• Reduce the volumes of manure created by changing waste management, handling practices, and feed
• Treat manure to kill pathogens, attenuate hormones and other organic contaminants, and stabilize
• Increase use of anaerobic treatment and composting to control odors, nutrients, pathogens, and
generate renewable energy.
• Reduce the use of antibiotics to stem the development of antibiotic resistant pathogens.
• Increase soil conservation methods to reduce runoff and erosion from fields to which manure has
been applied. Reduced tillage, terraces, grassed waterways, and contour planting offer conservation
• Install barriers such as riparian zones and wetlands to prevent manure-laden runoff from fields from
• Change barn ventilation and manure management and handling practices to minimize the airborne
release of stressors.
• Where economic factors work against making changes to CAFO management practices, eliminate
them or provide incentives for making such changes.
Additional research needs to be undertaken to develop a range of alternatives for managing CAFO
manure. The U.S. Department of Agriculture is engaged in research to address many of these questions,
especially with respect to nutrient issues. EPA intends to complement their efforts by working with them on
mitigation strategies for nutrients and, more importantly, focusing on pathogen, hormone and metal issues.
The environmental challenges posed by CAFOs are not insoluble. In some cases, simple
management of wastes in different ways will ameliorate some of the problems. More attention to good soil
management and application of wastes at phosphorus based agronomic rates will reduce loads of pollutants
reaching water bodies. Development of means to extract value from wastes will be needed to make
treatment feasible and reduce health risks. Nitrogen, phosphorus and methane are some of the potentially
valuable products recoverable from manures. The key problem for managing CAFO waste is one of
distribution of the manure from points of production to application sites in an economically viable manner.
Beyond manure management, new issues are emerging such as the environmental impact of
aquaculture and other intensive agricultural operations, the environmental effects of different types of
mortality management, and how to mitigate the hydrologic changes brought about by large CAFO
operations. These issues will be addressed in future versions of this RME.
2.1 Agricultural Sectors Considered in this Document
Hog, poultry beef, and dairy production are considered in this document. Although there are other
livestock production sectors that utilize intensive production methods, these represent the sectors most often
identified as the cause of water quality problems caused by animal agriculture (USEPA, 2001). The
recently promulgated rule addresses only these four agricultural sectors.
Animal production agriculture in recent years has evolved into a system with highly integrated
production. A company known as an integrator owns all of the components of production from the feed, the
animals themselves, and the slaughterhouse. Large numbers of animals are kept in barns or in the case of
beef cattle in feedlots that are owned by a farmer who is acting as an independent contractor for the
integrator. The farmer owns the facility where the animals are housed and fed. Typically, the farmer is
responsible for manure handling, safe storage, and disposal. This usually means that the manure is stored in
large piles or impoundments until it may be applied to the land. Manure has long been applied to
agricultural land as a fertilizer and as a means of soil improvement. Today, however, the large numbers of
animals housed in CAFOs generate waste on a scale that may overwhelm the capacity of the adjacent land
to absorb it. It is this excess manure that causes the environmental problems associated with CAFOs.
Manure production varies by animal species, diet, and age of the animal. An animal unit is a 1000-
pound animal, frequently taken as one market-weight beef animal. Each animal generates approximately 50
to 60 pounds of manure per day. From these figures, it may be seen that the waste load for a 1000 animal
unit facility is quite large. For example, a beef feedlot with 1000 animals produces about 21,000,000 Ibs of
manure per year.
3 MANURE PRODUCTION AND MANAGEMENT
3.1 Manure Quantities Among Animal Populations
Animal farms produce as much manure as small and medium-size cities. A farm with 2500 dairy
cattle is similar in waste load to a city of 411,000 people. Since about 1970, production of hogs, beef,
poultry, and dairy has become concentrated into fewer large units. Between 1982 and 1997, the most recent
years for which animal census data are available, the number of livestock has remained relatively constant,
but the number of farms has declined significantly. Dramatic changes have occurred in American
agriculture between 1982 and 1997, the most recent years for which animal census figures are available. The
most significant change is the shift from small farms to the much larger, concentrated animal feeding
operations (CAFOs). Table 3.1 shows a summary of changes in confined animal units from 1982 to 1997.
Table 3.1 Change in confined animal units, 1982 to 1997
All smaller size classes decreased
All smaller classes decreased
All smaller classes decreased
All smaller classes decreased
The definition of a CAFO listed in the regulation development document (USEPA, 2001) is used in
this document. A CAFO is an animal feeding facility that has more than 1000 animal units, or has between
300 and 1000 animal units and meets certain conditions or is designated a CAFO by the state, or has less
than 300 animal units and is designated a CAFO by the state. The smaller size facilities are designated
CAFOs primarily due to the potential the facility has for discharging pollutants to the waters of the United
States. Animals must also be present in the facility for at least 45 days. The CAFO neither stores nor grows
crops. Waste containment and disposal are also part of the CAFO designation. Poultry facilities are CAFOs
if they contain more than 55,000 turkeys; 100,000 or more broilers or hens with continuous overflow
watering; 30,000 or more hens or broilers with a liquid manure system; or 5,000 or more ducks. Designation
as a CAFO requires the facility to obtain a NPDES discharge permit.
In 1982, CAFOs comprised only 3% of all farm operations and more importantly, only 35% of the
total animal population. In 1997, CAFOs had risen to 5% of all farm operations and 50% of the animal
population. The circumstances associated with these changes in animal population are unique for each of
the four principal farm animal group categories; beef cattle, dairy cattle, hogs, and poultry. Table 3.2 shows
the changes in CAFO operations from 1982 to 1997, based on animal unit size classes.
These changes have been principally driven by economic factors, mostly economy of scale, that is, a
few large farm units have the potential to be much more cost and operationally efficient than many small
farm units. Perhaps the significance of the reduction in small farm units maybe made most dramatically by
comparing the numbers of farm units in 1982 to 1997. In 1982, there were 1,260,085 farms with fewer than
150 animals compared to 921,957 in 1997. This represents a 26% reduction in the total number of small
farm units. Meanwhile, the number of large farms with more than 1000 head of livestock increased from
5442 farms in 1982 to 8021 farms in 1997, which represents a 47% increase. And of course, the actual
"shift" in numbers of animal units is even more dramatic. There were 45.8 million animals on small farms
in 1982, but by 1997 this number was reduced to 34 million animals. Interestingly, this is a 26% reduction
in the total animal population for small farms. In contrast, large farm operations, that is, those with more
than 1000 animals, increased from 15.7 million in 1982 to 24.9 million in 1997, a 58% increase.
Table 3.2 Change in CAFO operations from 1982 to 1997
Other beef and
All smaller size classes decreased in number
Different parts of the United States are associated with major production facilities. See Figures 3.1
through 3.4 for locations of major animal production locales. The different animal production sectors are
vertically integrated to various degrees. Poultry production is most highly integrated, followed by pork,
dairy, and beef. The manure production by all of these animals is immense. Manure production varies by
the animal species, diet of the animal, and age of the animal. Table 3.3 presents some data comparing
manure production by the major animal groups.
Table 3.3 Manure production per 1000 pounds live weight, on an annual basis.
Tons per Year for
1000 Animal Unit
Based on 150 Ib avg. wt. per person producing 0.5 Ib of fecal material per day
On a 1000 pound live weight basis, each of these animals produces more waste than a human. A
CAFO with 1000 animal units of turkeys produces a waste load comparable to a city of 87,700 people. A
dairy CAFO with 1000 animal units is equivalent to a city of 164,500 people. The important difference
lies in the fact that human waste is treated before discharge into the environment, but animal waste is either
not treated at all or minimally treated by virtue of the storage methods used before disposal.
Poultry production (broilers, roasters, turkeys and eggs) is heavily concentrated in relatively few
states. Chicken production occurs in Georgia, Arkansas, Alabama, Michigan, North Carolina, Missouri,
Texas, and Delaware. Egg production occurs in Ohio, California, Pennsylvania, Indiana, Iowa, Georgia,
Texas, Arkansas, and North Carolina. Turkey production occurs in North Carolina, Minnesota, Virginia,
Arkansas, California, Missouri, and Texas. These states are those with the largest facilities. Other states
may have CAFO sized production units, but not be among the largest. Poultry are not usually calculated as
animal units due to the composition of their manure. Broiler manure has a N:P ratio of 3.6:1 and layer
manure has a N:P ratio of 2.7:1. The N:P ratio of turkey manure is about 2.7:1. Poultry manure is quite
high in phosphorus compared with other animal species. In some cases N and P are almost equal in
The total quantity of 120 million wet tons of poultry manure was estimated for 2001, and this figure
represents an increase of more than 80 % compared to 1982. Clearly, this quantitative increase is the
greatest change for all categories of animal fecal production. Some of the largest poultry operations are now
located in North Carolina, Arkansas, and the Delmarva peninsula. Today, most poultry production comes
from large concentrated egg or broiler operations. Delaware, as one example, may produce up to
250,000,000 chickens or more in one year. The waste generated contains more nitrogen and phosphorus
than may possibly be used as fertilizer in Delaware for crop production.
Manure production and manure handling is similar in broilers and turkeys, resulting in similar
nutrient concentrations. The floor is covered with moisture absorbing bedding and is ventilated. This
airflow removes ammonia and other gases leaving a nitrogen-depleted manure. Broiler manure as excreted
has a nitrogen content of 401 lb/yr/1,000 Ibs of animal weight (USDA, 1998); broiler house litter has a
nitrogen content of 27 lb/yr/1,000 Ibs of animal weight (USD A, 1992). Some of this decrease in nitrogen
may be explained by solubilization as when bedding is washed off the floor rather than scraped, as shown
by the decrease in phosphorus and potassium from 117 and 157, respectively, to 113 and 111 lb/yr/1,000 Ibs
of animal weight. The much larger percent loss of nitrogen results from off-gassing of ammonia.
Animal Units For Confined Poultry, 1997
Per County Or
200 fc 1,000
i.000 or mere
Figure 3.1. Poultry production distribution in the United States.
188.8.131.52 Broilers/Roasters and Turkeys
Broiler production in the United States was about 8.4 billion in 2001. The average cycle time for
broilers is about 47 days. The total amount of waste generated by broilers is estimated at 79 million wet
tons per year taking into account the cycle time of production. This estimate may be a high estimate
because it does not take into account the fraction of birds sold at much lower weights for different markets.
Turkey production also has multiple cycles per year. A good estimate is three production cycles of about 17
weeks each. The amount of waste generated is estimated at 21 million tons per year with three production
cycles. Most waste is handled as dry rather than liquid systems.
Turkeys Sold: 1997
1 Dot = 60,000 Turkeys
Source: 1997 Census of Agriculture
United States Total
Figure 3.2. Turkey production distribution in the United States.
The estimated number of layers in the United States is about 367,000,000. The life cycle of layers is
usually more than a year. The manure production by layers is estimated to be about 19 million tons per
year. It is possible to have layer flocks more than one year in age before market. The apparent maximum
for layers is about two years. Layer manure production often includes no bedding, it is handled as raw dried
manure or water flushed manure. Water flushing manure results in dilution with concurrent increase in
volume. Raw manure contains 308, 114, and 120 lb/yr/1,000 Ibs of animal weight of nitrogen, phosphorus
and potassium (USD A, 1998). Dry manure may lose up to 50% of the nitrogen content as volatile
ammonia. Poultry manure dries rapidly and may be scraped off of flooring and stored dry in stacks or
cakes. Dilution in lagoons and slurries may result in concentration reduction to as little as 10% of the raw
manure value (USDA, 1992).
Layers and Pullets 13 Weeks Old and Older - Inventory: 1997
1 Dot = 60,000 Layers and
Pullets 13 Weeks
Old and Older
United States Total
Source: 1997 Census of Agriculture
Figure 3.3. Layer and pullet distribution in the United States.
Hogs may live in several types of CAFOs throughout their life. Breeder facilities produce feeder
pigs from birth to about 15 pounds, nursery facilities raise the pigs to 40 to 60 pounds, and grower/finisher
facilities raise the pigs from 60 pounds to market weight of about 250 pounds. The total quantity of manure
produced by both breeding hogs and hogs for slaughter was 177 million tons (from 8.5 million swine) and
essentially this quantity was excreted in confined animal feeding operations. A variety of wet-handling and
dry-handling systems were used. There has been a dramatic shift in the location of confined hog farm
operations with North Carolina now being the most popular state with Iowa and Nebraska following behind.
Figure 3.4 shows the change in confined animal units from 1982 to 1997. There has been a large shift to
Change In Animal Units For Confined Swine
From 1982 To 1997
I I D*HT»S»* 1,000
Figure 3.4. Change in swine production distribution in the United States.
Figure 3.5 shows a modern hog confinement facility with a waste lagoon. The hogs may be
confined in pens as shown in Figure 3.6. In this type of facility the manure drops through the slatted floors
into channels that are periodically flushed with supernatant water from the lagoon. The floors are either
scraped or washed with water to move the waste into the subfloor channels. Demonstration projects have
been completed wherein the lagoon is covered with a synthetic material, and the lagoon is converted to an
anaerobic digester. Some farms have found it practical to recover methane from the lagoon to supply
electricity and heat for the farm.
Photo courtesy of USDA NRCS.
Figure 3.5. Swine confinement barns with lagoon.
Figure 3.6. Swine pens inside barn with slatted floors.
Photo courtesy of USDA NRCS.
Beef cattle generate about 21,000 Ibs of manure per animal per year, assuming one animal is one
animal unit. Beef production starts with cow/calf operations that produce feeder calves for feeding
operations. Calves are fed from birth to about 400 pounds. Then they are transferred to feeding operations
that feed them to market weight of about 1200 pounds. Veal calves are usually male calves fed in
confinement to about 450 pounds. The beef industry is located primarily in the central United States. The
largest operations are in the Great Plains states, Texas, Kansas, Nebraska, and Colorado.
There has been a large shift in cattle production to the central United States as shown in Figure 3.7.
Many areas have lost cattle production while Nebraska, Kansas, Oklahoma, and Texas have had great
increases in cattle production.
Change In Animal Units For Confined Fattened Cattle
From 1982 To 1997
I I D*cr««« 1,000
ta> . J -~~^ . _^
Figure 3.7. Change in cattle locations as of 1997 Census.
Figure 3.8 shows an aerial view of a large feedlot in Kansas. A waste lagoon is in the lower center
of the picture. There is an area above the lagoon that appears to be the inflow area for the lagoon, but may
also drain to unprotected streams. In large feedlots as shown in the figure, waste is generally scraped from
the surface of the lot and piled nearby until it may be moved from the site for field application. A limited
amount of treatment occurs in the piles due to self-heating of the material. Treatment by composting could
be implemented relatively easily with the manure scraped from feedlots. The compost could then be sold as
a value added product. The cost would be in the additional handling required to manage the composting
process. Veal calf production is more likely to use a fully liquid manure system to handle wastes because
the animals produce waste with higher water content and are held in confinement where water cleaning of
the barns is practiced.
Photo courtesy of USDA NRCS.
Figure 3.8. Aerial view of a feedlot in Kansas with a lagoon.
Perhaps one of the most important facts for the purposes of this document is that a total of 806
million wet tons of manure were shed by beef cattle in 1997 (only 13% of this quantity was excreted within
CAFOs, however). The quantity of manure produced by fattening beef cattle in CAFOs increased only 3%
in the fifteen-year interval from 1982 to 1997. Beef feedlot wastes vary widely due to climate, diet, feedlot
surface, animal density, and frequency of cleaning. Aged manure loses, on a dry weight basis, up to 60% of
the nitrogen, 50% of the phosphorus, and 35% of the potassium (Mathers, 1972) to volatilization, runoff, or
Dairy production is more evenly distributed due partially to the highly perishable nature of milk.
Large dairy operations exist in California, New York, Wisconsin, Pennsylvania, Minnesota, Texas,
Michigan, Washington, Idaho, Ohio, New Mexico, and Arizona, Texas, Idaho, New Mexico, and Arizona.
The distribution of dairy operations in the United States is shown in Figure 3.9. The highly perishable
nature of milk suggests a reason for the more even distribution of dairies than beef feedlots.
Change In Animal Units For Confined Milk Cows
From 1982 To 1997
Figure 3.9. Change in distribution of dairy cattle in the United States.
Some dairies practice good control of waste both for nutrient management and for good
environmental practice. Figure 3.10 shows a manure storage tank that gives the farmer good control over
waste management. Tanks as shown may not be feasible for large dairies with large animal populations due
to the volume of manure produced. Figure 3.11 shows a dairy farm with poor control of waste with
consequent poor nutrient and environmental practices. This farm is losing valuable nutrients to runoff and
possibly contaminating local streams with manure. Dairies may practice a variety of waste handling
methods. Large dairies with large lot areas may handle wastes by scraping the lots and piling the waste until
Photo courtesy of USDA NRCS.
Figure 3.10. Dairy farm with manure storage tank
it may be field applied or further processed by composting. Milk house waste is frequently combined with
the wash water and transferred to lagoons as a disposal mechanism separately from the feedlot waste. In
this case there are two waste systems. Dairies with cows housed in barns and little or no outside activity
usually have a combined waste system wherein the milk house waste, wash water and barn waste are
combined in a mostly liquid system.
Dairy cattle produced 187 million wet tons of manure in 1997, representing an increase of 25%
from the amount produced in 1982. Essentially this entire amount of fecal matter originated within CAFOs.
Dairy manure as excreted contains on average TKN 164, phosphorus 29, and potassium 102
pounds/year/1000 pounds of animal mass (Lander, 1998). Water washed systems with lagoon storage may
generate losses of 30-75% of the nitrogen (USDA 1992). The fecal matter produced within these operations
was handled and disposed of under a variety of wet and dry handling systems and in some instances
enclosed anaerobic digester systems have been employed so that methane gas production was optimized and
then captured for conversion into electrical energy.
Photo courtesy of USDA NRCS.
Figure 3.11. Dairy farm with poor manure management and detrimental impact on the environment.
3.2 Manure Characteristics.
After the animals have defecated, the manure begins changing characteristics. Manure is a dynamic
material, because it contains organic matter, nutrients, water, and microorganisms. Manure begins to lose N
as NHa almost immediately. Between defecation and application of manure to soil, volatile N losses may be
up to 90%. The N loss adversely affects the fertilizer value of the manure by reducing the N:P ratio. In
most cases, conservation of the N is beneficial economically. Loss of N as NHs also raises an air pollution
concern, as the N may be redeposited in watersheds where it becomes a pollutant. Esthetically, loss of N as
NH3 may create odor problems, leading to public disapproval of manure application, even though it is
agronomically beneficial. Ammonia losses are minimized by direct injection or incorporation of manure
into the soil surface. Up to 98% of N may be retained by injection. Maximum loss of N occurs when
manure is applied by high velocity sprinkler systems. The sprayers maximize air exposure of the waste and
consequently NH3 loss. Phosphorus is not generally susceptible to volatility losses.
The nutrient value of animal waste varies according to animal species and waste handling systems.
The nitrogen and phosphorus content of waste change greatly between excretion and field application. The
urea and ammonia content of waste is especially susceptible to loss to atmosphere. This represents a
potential economic loss as well as a transfer of a pollutant from one medium to another. Lagoon-based
systems tend to accumulate phosphorus in the sludge layer on the bottom. Periodic removal of the
supernatant disperses the N and P in the liquid phase. Eventually, the sludge layer will have to be removed
to regain storage capacity. Due to the increased P content relative to the supernatant, the land area required
for disposal will be greatly increased to prevent overloading with P. Examples of waste nutrient content are
shown in Table 3.4.
Table 3.4. Nitrogen and Phosphorus Content of Animal Waste
As excreted, lb/1000 Ib/year
As applied, lb/1000 Ib/year
The wide range of nutrient content observed reinforces the need for the individual CAFO operator to
have periodic manure analyses done. An annual analysis will provide adequate information for planning
application for crops.
3.2.1 Physical Properties
The physical properties of manure produced by the main commercial animal species have some
common and some individual characteristics. Poultry manure is drier upon excretion than manure produced
by any other common species. The characteristics of manure of most interest for the purposes of this
document include the moisture content, nutrient content, COD, and BOD representative of the different
animal manures. Table 3.5 summarizes basic data on manure characteristics.
Table 3.5. Characteristics of animal manure based on 1000 pound live weight.
The effects of excess nutrient release into the watershed may cause eutrophication of water bodies
with consequent degradation of potential uses of the water. Harmful organisms may bloom in response to
the nutrient input causing problems with fisheries and human health. And in the case of the Mississippi
River ammonia inputs to the Gulf of Mexico have led to the development of extensive anoxic zones.
Control of nutrient loss is important to management of animal wastes.
3.2.2 Nutrient Content and Form from Poultry
184.108.40.206 Layers, Broilers, and Turkeys
Poultry is made up of three sub-types: layers, broilers, and turkeys. Broilers and turkeys are fed to
optimize growth and development, while layers are fed to maximize egg production. Manure produced by
these groups reflects these differences as well as differences in housing practices.
Manure production and manure handling is similar in broilers and turkeys, resulting in similar
nutrient concentrations. The floor is covered with moisture absorbing bedding and is ventilated. This
airflow removes ammonia and other gases leaving a nitrogen depleted manure. Broiler manure as excreted
has a nitrogen content of 401 lb/yr/1,000 Ibs of animal mass (USDA, 1998); broiler house litter has a
nitrogen content of 27 lb/yr/1,000 Ibs of animal mass (USD A, 1992). Some of this decrease in nitrogen may
be explained by solubilization as when bedding is washed off the floor rather than scraped as shown by the
decrease in phosphorus and potassium from 117 and 157, respectively, to 113 and 111 lb/yr/1,000 Ibs of
animal mass. The much larger percent loss of nitrogen results from off-gassing of ammonia.
Layer manure production often includes no bedding, and it is handled as raw dried manure or water
flushed manure. Water flushing manure results in dilution with a concurrent increase in volume. Raw
manure contains 308, 114, and 120 lb/yr/1,000 Ibs of animal mass of nitrogen, phosphorus, and potassium
(USD A, 1998). Dry manure may lose up to 50% of the nitrogen content as volatile ammonia. Poultry
manure dries rapidly and may be scraped off from flooring and stored dry in stacks or cakes. Dilution in
lagoons and slurries may result in concentration reduction to as little as 10% of the raw manure value
(USD A, 1992).
220.127.116.11 Nutrient Content and Form from Swine
Swine manure is typically collected in lagoons, pits, or both (Svoboda 1995). Nitrogen loss in the
water fraction of the lagoons due to aeration may be as much as 76-84% of the original nitrogen content.
Phosphorus and potassium losses to accumulation in sludge may be 78-92% of the phosphorus and 71-85%
of the potassium (Jones and Sutton, 1994). The phosphorus and potassium lost from the aqueous stream are
found in lagoon sludge.
Generally speaking, boars and larger swine produce manure with a higher nutrient content. Values
reported here are for grower-finisher operations as these are more representative of the life-long manure
production of the swine. Typical values are nitrogen, 166; phosphorus, 48; and potassium, 117 lb/yr/1,000
Ibs of animal mass. Water-washed floors result in wet manure, which is often stored in lagoons.
18.104.22.168 Nutrient Content and Form from Cattle
Average dairy manure as excreted contains TKN 164, phosphorus 29, and potassium 102 lb/yr/1,000
Ibs of animal mass (Lander, 1998). These wastes are typically water-washed and stored in lagoons with
concurrent loss of 30-75% of the nitrogen content (USDA, 1992).
Beef feedlot wastes vary widely due to climate, diet, feedlot surface, animal density, and frequency
of cleaning. Feedlots are typically scraped and the resulting waste is stored on the ground. Aged manure
loses, on a dry weight basis, up to 60% of the nitrogen, 50% of the phosphorus, and 35% of the potassium
(Mathers, 1972) to volatilization, runoff, or leaching.
3.3 Manure Management Practices
3.3.1 Wet Manure Management
Liquid or slurry systems include wet barn washing, under-building or lagoon storage followed by
spray application, injection, or gate and channel application onto the land. Liquid manure systems handle
material with solids content below 10%. Gravity flow systems work well for movement of wastes from
production to storage facilities, such as lagoons. Operations that require pumping to move wastes should
have solids content of less than 4%. Liquid wastes are amenable to treatment in digesters. The digesters
may be well engineered and controlled systems to increase efficiency, or enhanced lagoon storage to enable
a lower intensity treatment, with longer treatment time. These systems are most amenable to recovery of
fuel value from methane production. Swine and dairy operations commonly use wet manure management
and are therefore potentially at risk from nitrogen percolation to groundwater and airborne stressor
transport, especially if wastewater is sprayed. Liquid systems are described in more detail in the land
3.3.2 Dry Manure Management
Solid manure systems include mechanical scraping of waste to clean out barns, pile storage and land
application using a manure spreader, either truck-mounted or tractor-drawn powered spreaders. Dry
systems include the manure plus any bedding material used. Typical bedding may be wheat straw, corn
stover, corn cobs, sawdust, or any absorbent material. The bedding material absorbs water and changes the
C:N ratio of the manure. The resultant material may then be suitable for composting with little need for
adjusting carbon content.
Poultry and beef feedlot operations use dry manure management and so are more at risk from
phosphorus application to land. Many CAFOs occupy only enough land for their day-to-day operations.
The amount of manure produced in the CAFO may well exceed the capacity of the available land to absorb
it. This is especially true when applications are based on phosphorus needs of crops rather than nitrogen.
Offsite manure transfer may be a valuable way to expand the disposal area available. However, adequate
record keeping and nutrient management is essential to avoid excess application to fields.
Typically, the smaller operations use familiar manure spreaders to distribute the manure in farm
fields. Manure is loaded from the barn using a tractor-mounted scoop into a power driven spreader box or
flail spreader. The spreader is driven to the field and the load distributed onto the land. The solid spreaders
handle manure that is about 20 to 25% dry material, sometimes less. The material may be stacked with little
or no liquid seepage. This type of manure is most easily treated by composting, should treatment be
required before distribution. Incorporation of manure should be done as soon as possible after application to
ensure N retention. Incorporation may not be done if the manure is applied to standing crops. The primary
benefit of this system is relatively low cost for equipment. Evenness of distribution is not easily obtained.
Timing of application is not generally done with nutrient management in mind. The small operator spreads
manure when other activities are not pressing. Common times are: fall after harvest of corn and soybeans,
winter, spring after planting is done, and summer after wheat is harvested. The largest risk would come
from the winter application on frozen soil. Incorporation would not be feasible, and upon spring thaw and
rainfall, runoff could produce significant losses of material to receiving water.
4 WATERSHED STRESSORS IN CAFO WASTE
The pollutants potentially leaving the CAFOs may affect watersheds directly or indirectly. The
most often cited stressors affecting watersheds include nutrients, pathogens, sediments, EDCs, antibiotics,
and metals. Direct effects occur when wastes flow directly into a receiving water as a result of poor storm
water management or catastrophic failure of containment facilities. Indirect effects occur when wastes have
been applied to a field and are subsequently moved into waterbodies by runoff after rainfall, percolation into
groundwater with subsequent entry into streams or tile drain lines, wind driven movement, or volatilization
and redeposition as in the case of ammonia.
The nutrient content of the manure generated on the CAFO is one of the most significant problems.
Nitrogen in the waste may be transferred in the environment two ways. Ammonia may be volatilized from
the waste directly into the air and generate odor and downwind deposition problems. Nitrate generated in
the soil applied waste may enter surface or groundwater and may exceed the national drinking water limit of
10 mg/L to cause health problems in young children.
Phosphorus in waste may easily exceed crop requirements for a given year on a localized basis. If
continual applications are made year after year, the soil becomes saturated with P and the potential for
runoff losses and groundwater losses greatly increase.
The soil, if eroded will contribute to stream degradation by eutrophication. Erosion of soil onto
which manure has been applied, may contribute to other environmental problems in waterbodies. Organic
matter exerts an oxygen demand leading to a depression of dissolved oxygen. Solids, as either manure
particles or eroded soil particles, increase the sediment load in streams and may unduly shade some parts of
the stream. Other habitat effects will be associated with increased sediment load.
Microorganisms associated with manure may present a significant risk to health. The population of
several known pathogens may be quite high in manure. Runoff from land application sites may carry large
numbers of organisms into streams. Recreational use of the streams may then bring people into direct
exposure to large numbers of potentially pathogenic microorganisms. Several disease outbreaks have been
associated with manure contamination of water or food that has been contacted by manure.
There are also concerns associated with the potential metal content of poultry or swine waste. Trace
levels of arsenic are added to poultry feed to promote growth. Similarly, copper is added to swine feed for
growth promotion. Antibiotics, hormone compounds, and pesticides are found in animal wastes, and the
environmental effects of these compounds are largely unknown. The following sections are meant to
summarize the most pertinent literature concerning nutrients and other stressors from CAFO manure. The
literature in the area of nutrients and nutrients as pollutants is overwhelming. This is an attempt to limit the
literature review to the citations that have the most impact on EPA's mission.
"Livestock wastes, which for present purposes are defined as liquid and solid excreta with the
associated remains of bedding and feed and sometimes with water added, have long been ranked among the
farmer's most valuable resources. For traditionally, the fertility of his land has depended in very large
measure on the supply of such waste, sometimes dropped in his field by grazing animals or sometimes
stabilized in the steading into farmyard manure by the addition of straw. In the days of the agricultural
revolution the efficiency of the yards as a 'manure factory' was one of the primary criteria of farmstead
design. More recently and more drastically, a variety of agricultural changes have combined to convert,
under certain circumstances, this potential asset (manure) into an increasing liability. The agricultural
changes result from growing economic pressures to increase the animal outputs by an increase in the
number of livestock carried per unit of land." (ARC 1976)
Animal waste contains nitrogen in organic and inorganic forms. The inorganic form is ammonia,
and organic forms include urea and an array of organic compounds. Nitrogen compounds may move in a
watershed in air, surface runoff, or through percolating groundwater. Any form of nitrogen may have an
impact on a watershed because it is a major plant nutrient. Ammonia is immediately available to plants as
ammonium ion. Ammonia may move as an air pollutant after volatilization from animal waste. In the soil,
ammonia enters solution as ammonium ion that may be held on soil colloid exchange sites. Ammonium is
formed when organic-N such as urea is metabolized either aerobically or anaerobically to NHs that ionizes
in water to ammonium. Ammonia may lead to eutrophication, excessive oxygen demand in surface waters
and fish kills, reduced biodiversity, objectionable tastes and odors, and growth of toxic organisms. Both
forms of ammonia, NHa and NH4+, are toxic to aquatic life, although NHa is more toxic to fish. Ammonia
may be converted by nitrification to nitrite and nitrate. Nitrite is toxic to fish and most aquatic species.
Nitrite does not accumulate in the environment because it is rapidly oxidized to nitrate naturally by aerobic
bacteria. Nitrate is highly mobile and may easily leach downward through the soil profile to an aquifer.
Nitrate is the most widespread agricultural contaminant in drinking water wells (U.S.EPA, 1998). A
drinking water maximum contamination level (MCL) of 10 mg/L has been set for nitrate-N based upon its
role in the "blue baby syndrome" or methemoglobinemia. Nitrate may be converted to nitrite by nitrate
reducing bacteria found in the low acidity infant stomach. Nitrite may then attaches to fetal hemoglobin in
human infants forming methemoglobin, which is ineffective as an oxygen carrier. This toxicity, if not
treated, may be fatal (Goldstein et al., 1974). Figure 4.1 depicts processes primarily responsible for
transformation of nitrogen compounds in sediments at the bottom of lagoons (collection ponds) or in a
topsoil layer treated with animal manure.
Soil profile characteristics and management practices may significantly affect leaching of nitrate and
ammonium in feedlots and crop fields (Saint-Fort et al., 1995). Whereas runoff is the primary mechanism
for the transport of sediment bound and solution phase ammonium, groundwater flow is the primary
contributor of nitrate to surface water from agriculture. (Follet, 1995). Spatial variability of nitrate in
ground water and temporal fluctuation are related to seasonal recharge and hydrologic variations in the
region (Halberg, 1986). High concentrations of nitrate in groundwater are associated with high permeability
soil and aquifer material, such as permeable sand and gravel, karst limestone, or fractured rock (Hitt et al.,
1999). In these landscapes, manure applied as fertilizer is susceptible to relatively rapid infiltration, thus
contaminating ground water with nitrogen and/or phosphorus.
SOD controlled diffusion
Figure 4.1. Depiction of carbon and nitrogen cycles in soils or sediments.
Leaky lagoons and below grade storage facilities are potential sources of nitrogen compounds that
may enter groundwater. As structures age, the integrity of the walls and bottoms of the lagoon may be
penetrated by burrowing animals, or the lagoon walls and bottoms may develop cracks from wetting and
drying cycles as the water level in the lagoon changes (U.S. EPA, 2001). Rupture of lagoon seals may be
attributed to drying of exposed embankments when lagoon levels drop or gas release from microbial activity
in soil beneath the seal (Ciravolo et al., 1979: Parker et al., 1999). Short-circuits to natural filtering, such as
uncapped or improperly capped wells and infiltration in vegetated filter strips adjacent to lagoons are
potential sources of groundwater contamination (U.S. EPA, 2001). Groundwaters in areas of sandy soil,
karst formations, or sinkholes are particularly vulnerable to nitrogen infiltration. Leaching of ammonia
compounds is generally not a significant transport mechanism, because ammonium may be sorbed to soils,
fixed by clay minerals and organic matter, or transformed into organic forms by soil microorganisms
through the process of immobilization (Follet,1995). Mineralization is a process whereby organically bound
nitrogen is converted to inorganic mineral forms, (NH4+ and N(V). Legume crops may fix atmospheric
nitrogen by transforming (N2) to ammonia. Ammonium adsorbed onto soil below liners in abandoned dry
lagoons, through nitrification, may produce nitrate (Ham, 1999) that is potentially available for leaching into
the deep subsoil and ground water. Two modes may dominate transport of pollutants in soils: 1) rapid
advection through macropores; and 2) slow percolation through the soil matrix. The first transport mode,
which is promoted by gravitational forces through macro-channels, is also referred to as preferential flow
(Figure 4.2). The second mode is much slower and is governed by gravity drainage and capillary forces at
\ IntersHUai (pore-water)
Figure 4.2. Diagrammatic illustration of preferential flow through macropores and interstitial (pore-water) flow in the soil
work through interstitial pore space. Preferential flow through macropores in soils beneath a waste lagoon
may transport NH4+ or nitrate to ground water. Subsurface runoff and tile drainage are other transport
pathways for nitrogen to surface waters.
Percolating water and leachate below lagoons may transport nitrate to ground water. Preferential
flow through macropores and karst formations are also transport pathways to ground water. In heavily tile-
drained watersheds most of the N added to surface water originates from tile drainage (Kovacic et al., 2000).
In some areas nearly half of the applied fertilizer nitrogen may be discharged with tile-drainage water
(Kanwar et al., 1983).
Nitrogen retention in the soil by adsorption of NH4+ onto soil colloids may constitute a source of
NOs" to ground water (Ham, 1999). Urea and organic forms of N are also susceptible to leaching to ground
water. Under anaerobic conditions, nitrate may be reduced to N2 by denitrification, a primary process in
reducing nitrate in ground water (Crandall, 1999). Denitrification occurs in the absence of dissolved oxygen
and in the presence of chemically reduced compounds such as organic carbon or some divalent metals.
Phosphorus exists as both organic and inorganic forms in animal waste. Inorganic phosphate in
manure is easily adsorbed to soil particles, and thus has limited leaching potential. Organic P compounds are
generally water soluble and subject to leaching (Sweeten, 1991).
Organic phosphate may easily be metabolized to inorganic phosphate that is the form that is useful
as a nutrient. Inorganic phosphate in surface water is a major contributor to eutrophication. Because most
surface water plant and algal growth is rate limited by phosphate level, pollutant phosphate is of particular
concern. In concentrations over 1.0 mg/L phosphate may inhibit floe formation in drinking water treatment
plants (Bartenhagen et al., 1994).
Phosphorus is much less susceptible to leaching because of its adsorption onto soil particles and
therefore, poses less of a threat to groundwater than nitrate. Adsorption-desorption reactions in the soil
regulate the rate at which P may be released (Siddique et al., 2000). Phosphorus accumulation in topsoil
from animal waste and fertilizers constitutes a sediment problem more than a groundwater problem because
P binds to the most erodible soil components (clay, organic matter, and oxides of Fe and Al)(Sims et al.,
1998). However, if continual applications are made year after year, the soil becomes saturated with P and
the potential for runoff losses and groundwater losses increases greatly. Phosphorus leaching may occur in
sand soils where over-fertilization and/or excessive use of organic waste have increased soil P levels in
excess of crop requirements (Sims et al., 1998). Preferential flow through macropores (e.g. soil cracks, root
channels, earthworm borrowings) may transport a significant part of the phosphorus by suspended soil
material to tile drains (0ygarden et al., 1977). Leaking from lagoons is also a likely source for groundwater
contamination by phosphorus.
Environmentally significant export of anthropogenic P from agricultural soils by subsurface runoff
begins with downward movement of P, either by slow leaching through the soil profile or preferential flow
through macropores (e.g., soil cracks, root channels, earthworm borings). Dissolved inorganic P
concentrations in subsurface runoff in artificial drainage systems may be higher than values associated with
eutrophication of surface waters (Ryden et al., 1973, and Sims et al., 1998). P leaching may occur in deep
sand soils, in high organic matter soils, and soils where over-fertilization and/or excessive use of organic
waste have increased soil P values well above those required by crops. Leaching potential of P increases in
soils with low concentrations of soil constituents that are primarily responsible for P retention, such as clays,
oxides of Fe and Al, and carbonates (Sims et al., 1998). Mineralization of organic P and preferential flow
through macropores and cracks caused by conservation tillage systems increase P concentration in drainage
waters, including sediment-bound P.
4.1.3 Mineral Salts
Mineral salts of major concern in animal waste include the cations sodium, calcium, magnesium,
and potassium and the anions: chloride, sulfate, bicarbonate, carbonate, and nitrate. These mineral salts,
when applied repeatedly, may accumulate and increase soil ionic strength to levels that are toxic to plants
and animals. Runoff may contribute to surface water salinization and leaching salts may affect ground
water quality. Trace elements such as arsenic, copper, selenium, and zinc are often added to animal feed as
growth stimulants and biocides. These when land applied may accumulate and adversely effect both human
and ecologic health.
Animal manure is a potential source of pathogens. The organisms of concern in animal waste may
be bacteria, fungi, protozoa, viruses, or worms. When released into the environment, these organisms may
adversely effect human and animal populations. Although CAFOs are not the only source of these
microorganisms, they are a major source of pathogenic contamination in most watersheds (Pell, 1997).
Indeed, of the water bodies evaluated by the states, as required by the Clean Water Act, 36% of rivers were
unfit for swimming and/or fishing as the result of pathogenic contamination largely attributed to CAFO
operations (USEPA, 2001). In addition, the source waters from which drinking water is obtained for up to
43% of the United States comes from waters that are impaired by pathogenic contamination from CAFO
operations (USEPA, 2001). About 15% of the population of the United States obtains drinking water from
individual wells. When wells are located in areas hydrologically connected to CAFO operations,
individuals using these wells may be exposed to pathogenic organisms present in the groundwater. Without
purification, this may result in illness. CAFOs are likely to release pathogens into the environment for
several reasons. First, because of the large number of animals kept in CAFO operations, the likelihood that
one or more of the animals is infected with one or more pathogens is very high (Clinton, et al. 1979, Pell,
1997, Wesley et al. 2000). Second, because of the large volume of waste produced, manure may not be
disposed of on-site in such a way that the pathogens will be killed or inactivated. Without treatment to
reduce pathogen loads, storage and disposal practices will only serve to disseminate the microorganisms
more widely in the environment.
Conventional water treatment is adequate to prevent the entry of bacterial contaminants into public
drinking water supplies. Protozoan contaminants are usually in the form of cysts that are very resistant to
chlorination. Drinking water treatment needs to be designed and operated properly to remove
Cryptosporidium oocysts (Patania et al., 1995). Filtration through sand filters is usually necessary to
remove protozoan cysts.
For the purpose of this RME only selected pathogenic organisms known to have a significant impact
on human health or the environment and that are likely to come from CAFOs will be discussed. Before
beginning a detailed discussion of these organisms, however, we will first discuss pathogenic organisms in
general, their effects when released into the environment, and finally, relate the organisms to the CAFO
species that is most likely the reservoir for each organism.
4.2.1 Pathogens of Concern at CAFOs
More than 130 microbial pathogens have been identified from all animal species that may be
transmitted to humans by various routes (USDA, 1992; USEPA, 1998). Of these, 24 pathogens are likely to
originate from animal populations. Historically, fewer than ten have caused significant disease outbreaks
among humans. Potential environmental exposure to human populations extending beyond animal handlers
exists for cryptosporidiosis, giardiasis, campylobacteriosis, salmonellosis, colibacillosis, leptospirosis,
listeriosis, and yersiniosis; and many large-scale outbreaks have been attributed to each of these pathogens.
Pathogens include bacteria, fungi, viruses, helminths (parasitic worms), and protozoa. Not all pathogens are
present at every CAFO. Understanding the distribution of pathogenic organisms makes it easier to design
strategies that will reduce risk. Table 4.1 lists commonly occurring diseases and the animals that are
associated with these diseases. A general discussion of each of these classifications follows.
Bacteria are single-celled, prokaryotic microorganisms that are capable of causing disease in larger
organisms, although most bacteria are non-pathogenic. They may grow and proliferate within higher
organisms and are shed in feces. The presence of large volumes of feces in and around animals in CAFOs
provides a breeding ground for many bacteria. The bacteria that have been shown to have the widest
environmental impact when released into the watershed include E.coli 0157:H7, Salmonella.,
Campylobacter, Yersinia, and Listeria. The primary concern is that disease outbreaks may occur after
Table 4.1 Diseases and animals commonly identified as sources of the causative organisms.
contact with these organisms via swimming, eating shellfish, eating contaminated food, or drinking
Fungi are either single celled organisms or multicelluar, eucaryotic organisms that may cause disease
in other organisms. Fungal diseases are commonly difficult to treat and may persist for long periods of
time. Common diseases include candidiasis, histoplasmosis, aspergillosis, and dermatomycosis.
Viruses consist of nucleic acid molecules packed within a surrounding protein coat. Viruses only
actively replicate when they have invaded a host cell. The virus genes take over the host cell metabolism to
make more virus particles at the expense of the host cell. There is some evidence that reoviruses and many
enteroviruses may be transmitted from animals to man. Also, a number of rotaviruses are known to cause
diarrhea in both cattle and humans. Among farm workers, vesicular stomatitis is frequently transmitted
from sheep to humans, and the potential spread of cow pox virus (vaccinia) to humans was the basis for the
classical immunological practice of vaccination. Present day surveys indicate that rabies is more likely to
be transmitted from cattle to man than from either cats or dogs. At this time much less specific information
is known about the actual transmission of viral diseases from livestock to humans.
Intestinal parasitic worms occupy space in the host organism's intestinal tract. The worms absorb
nutrients from the host and thereby create a burden on the host. The prevalence of worms has declined in
the United States. Transmission is frequently through oral-fecal routes or from exposure through food
contaminated with manure.
Cryptosporidiumparvum. Among humans Cryptosporidiosis is caused by the protozoan parasite,
and it has recently been determined that there are two separate genotypes, Type 1 (human) and Type 2
(bovine), that can cause human infections. For the Type 2 genotype, the infective dose may vary from 10 to
1000 oocysts and infection is generally more severe in children and immuno-compromised individuals.
Virtually all cattle herds carry some level of cryptosporidiosis, and persistence and spread in the
environment is aided by passive transfer from rodents and birds. Infected animals can shed more than one
billion oocysts per gram of manure. Many large-scale waterborne outbreaks have occurred in the United
States. Conventional drinking water disinfectants such as chlorine and chlorine dioxide are not effective in
killing C. parvum. The standard water treatment processes of coagulation, flocculation, and filtration are
thought to be effective in removing this parasite when operating normally.
Giardia lamblia: Giardiasis among humans may be traced to many possible sources including
foodborne and waterborne transmission. It has been estimated that 2% of the population has been infected
with this organism, and more outbreaks result from a waterborne origin than those caused by contaminated
food sources. Wild animal populations such as deer, beavers, and bears may be the cause; however, more
than 50% of dairy and beef cattle herds in the United States are infected with this organism. Infection may
result from ingestion of only one oocyst, and once diarrhea occurs it may last up to two weeks. An ELISA
assay for the detection of oocysts is readily available, and a vaccine for giardiasis is available for dogs and
4.2.2 Disease Descriptions
Some of the diseases involved in significant waterborne disease outbreaks are summarized below.
Enterohaemorrhagic Colibacillosis (Escherichia coli (EHEC) O157:H7). There are many
serotypes of Escherichia coli from animal sources that may infect humans. This group of diseases is
referred to as colibacillosis. CAFOs, specifically cattle operations, may be sources of the organisms.
However, among the various enteropathogenic and enterotoxigenic forms, E. coli O157:H7 clearly has the
most serious manifestations. The hemorrhagic-toxigenic symptoms may often lead to death in 5-7% of
infected individuals. The infective dose is thought to range between 10 and 1000 organisms.
Contamination with cattle feces is known to be the most likely source of infection in the U. S. with
foodborne infections ranking highest; however, waterborne and recreational exposure is also associated with
this disease. Interestingly, outside of the United States isolation of cultures of E. coli O157: H7 is
associated with sheep. Although swine and poultry carry many strains of E. coli, the specific Strain
O157:H7 has not been isolated from these farm species. Three E. coli outbreaks (one in Montana in 1995,
one in Illinois in 1996, and one in Connecticut in 1996) were traced to organic lettuce growers. It is
suspected that the lettuce was contaminated by infected cow manure (Nelson, 1997).
Campylobacteriosis (Campylobacter jejuni): This organism is the leading cause of bacterial
diarrhea in the United States, the most common source being chickens, or more correctly, fecal
contamination of poultry meat. This organism is also commonly transmitted by cattle, birds, and even flies.
While the digestive tract of chickens contains many species of Campylobacter, it appears that most human
infections are caused by four thermophilic strains of this organism. C. jejuni causes a watery diarrhea that is
only occasionally bloody. Other symptoms include fever, abdominal pain, nausea, headache, and muscle
pain. The illness usually lasts two to five days, but reinfection is common and treatment with antibiotics
(preferably erythromycin) is not usually necessary. Surveys show that 20-100% of retail chickens are
contaminated. When human outbreaks occur they are usually small (less than 50 individuals) although one
large outbreak (2,000 people) occurred in Bennington, VT in 1978. Guillain-Barre syndrome may occur as
a sequel to this infection as well as meningitis, recurrent colitis, and acute cholecystitis, but these
occurrences are rare. Although chickens are the primary animal species associated with this organism,
transmission from infected milk is relatively common.
Yersiniosis (Yersinia enterocolitica): This organism is a gram-negative rod that is often isolated
from wounds, feces, sputum, and mesenteric lymph nodes. CDC estimates that 17,000 cases occur annually
in the U.S. It is one of the three most significant microbes than can originate from large swine operations.
Yersiniosis is frequently characterized by diarrhea and/or vomiting, fever, and abdominal pain. Similar to
Salmonellosis, postenteritis arthritic conditions occur in 2-3% of the affected individuals.
Listeriosis: The CDC estimates that approximately 1600 cases of listeriosis occur each year with
500 resulting in death. It is believed that cattle that are being fed silage are much more likely to harbor this
organism. Two separate clinical disease patterns may follow infection with Listeria monocytogenes. The
more mild form is commonly referred to as gastrointestinal listeriosis and is characterized by a rapid onset
of diarrhea, abdominal cramps, and nausea. The more serious form of the disease is referred to as listeriosis.
Symptoms include septicemia, meningitis, encephalitis, and intrauterine or cervical infections in pregnant
women resulting in spontaneous abortion (2nd or 3rd trimester), or a stillbirth. Gastrointestinal symptoms
have been epidemiologically associated with use of antacids which significantly lower the infective dose.
Cryptosporidiosis: Many large-scale waterborne outbreaks have occurred in the United States.
Particular attention is focused on the outbreaks in Milwaukee, WI and Carrollton, GA in which 400,000 and
17,000 persons, respectively, were infected. In another incident in Maine, a few hundred children were
sickened by Cryptosporidium. The source was fresh-pressed apple cider made from apples gathered from a
cow pasture (Millard et al., 1994). Conventional drinking water disinfectants such as chlorine and chlorine
dioxide are not effective in killing C. parvum. The standard water treatment processes of coagulation,
flocculation, and filtration are thought to be effective in removing this parasite when operating normally.
Giardiasis: Giardia lamblia: See Above
4.2.3 Effects of Pathogen Pollution
There is ample evidence that pathogens from agricultural operations have caused human disease
outbreaks in the past. Ecological damage has also been indicated. Spread from animal to animal at the
CAFO is a concern that individual operators have responded to with thorough periodic cleaning usually
after one group of animals is sent to market and before another arrives.
Although more is known about the human diseases that may be caused by pathogens released from
CAFOs, this section will also discuss the ecological effects of pathogens released into the environment.
An expert panel recently meeting on "Emerging Microbiological Food Safety Issues:
Implications for Control in the 21st Century" concluded that control of manure has become a critical issue.
Properly treated manure may be an effective and safe fertilizer, but untreated or improperly treated manure
may contain pathogens that may reach fresh produce in the field or nearby water supplies.
The following text, tables, and references provide supporting evidence that farm animals held in
CAFOS serve as an important reservoir for significant human pathogens and there are documented cases
where serious disease outbreaks have occurred as a result of these animals' manure containing pathogens.
Table 4.2 shows examples of manure-related human epidemics. A brief summary of each incident follows.
These outbreaks involved E. coli O157:H7, Campy lobacter, and Cryptosporidium parvum. All cases
summarized below resulted in serious illness and even some deaths.
Table 4.2 Examples of Manure-Related Human Epidemics
Maine & Others
E. coli O157:H7 &
Campy lob acter
E. coli O157:H7 &
E. coli 0151 -HI
E. coli 0151 HI
E. coli 0151 HI
2 deaths, 116
243 cases, 4
Runoff from farm
runoff from farm
storm runoff from
spread in apple
used in fields
water line breaks
in farm community
Valcour, J. E.,
et.al. Emerg Inf
Dis., March 2002
JAWWA, 88; 76-86
Eng. J. Med.
4.2.4 Human Diseases: Examples of Manure-Related Human Epidemics, Case Studies of Problems
and Potential for Problems with Pathogens in Animal Manure
22.214.171.124 Walkerton, Ontario
In May 2000, at Walkerton, Ontario, Canada, 2300 people were infected with E. coli O157:H7, and
a smaller number were co-infected with Campylobacter jejuni. There were seven deaths, and more than 100
people were hospitalized. A direct link was made to cow manure as the source of the pathogens since a
pasture occupied by cattle was located near the ground water source for the city's water supply.
126.96.36.199 Washington County Fair, New York
An outbreak of Escherichia coli O157:H7 and Campylobacter spp. also occurred among attendees of
the Washington County Fair, New York in 1999. In this outbreak 116 cases were confirmed, 65 people were
admitted to the hospital, 11 children developed HUS (Hemolytic Uremic Syndrome) and 2 children died.
The link to cattle manure as the source was primarily through the isolation of these organisms from a
shallow well on the fairgrounds and the knowledge that this organism is frequently found in cattle feces.
188.8.131.52 Carrolton, GA
In 1987 an estimated 13,000 people became infected with Cryptosporidiumparvum due to a
malfunction of the drinking water treatment plant. In addition to problems with the coagulation flocculation
system, the filtration system was shut down periodically without backwashing the filters prior to each re-
start. This failure of process control allowed C. parvum oocysts to freely pass through the filtration process.
Carrolton, Ga. was the initial large-scale outbreak of crytosporidiosis in the United States.
184.108.40.206 Wilshire, Swindon, and Oxfordshire, England
An outbreak occurrd in Wilshire, Swindon, and Oxfordshire in January 1989, in which 516 cases
were recognized, and 8% of the cases required hospitalization. The cause was traced to drinking water, and
much emphasis was placed on the fact that the Thames River in this region drained cattle grazing areas.
Extensive examination of the water treatment process was carried out, and a boil water order was issued.
The outbreak(s) followed periods of heavy rainfall, and this factor supported the hypothesis that cattle
manure was a source of the oocysts.
220.127.116.11 Bradford, England
In the community of Bradford, England, a city of 50,000 residents, 125 cases of cryptosporidiosis
occurred over a 7-day period. All cases were confirmed by laboratory examination for oocysts. The
average oocyst concentration in the city water supply was 0.019/L, and the outbreak occurred following a
storm event in which excess water was draining from agricultural fields.
18.104.22.168 Milwaukee, Wisconsin
The largest waterborne outbreak of disease occurred March-April 1993 and resulted from a breach in
treatment in one Milwaukee, Wisconsin water treatment plant. This event was responsible for 400,000
cases of illness and 87 deaths, with the deaths occurring among the immuno-compromised segment of the
population. Both animal manure and material from a community wastewater treatment plant were
implicated as likely causes of this epidemic.
There is evidence that a 1993 E. coli outbreak in Maine was the result of manure applications to a
22.214.171.124 Sakai City, Japan
A massive outbreak of enterohemorrhagic E. coli O157:H7 infection occurred in July 1996 in Sakai
City, Japan. The outbreak affected 12,680 school children and was caused by E. coli O157:H7. The
pathogen was present in radish sprouts that the children consumed in a school lunch program. This is the
largest outbreak due to this organism. From the original 12,680 children, 425 were treated at a local
hospital, 121 developed the hemolytic-uremic syndrome. Three children died. This outbreak may be linked
indirectly to cattle manure since the fields where the alfalfa sprouts were grown had been fertilized with
126.96.36.199 Cabool, Missouri
In December 1989 and January 1990 contamination of the city water supply in Cabool, Missouri
resulted in 243 cases of Salmonella typhi infection and resulted in 4 deaths. Cabool, MO is located in an
agricultural area of Missouri with large populations of beef and dairy cattle in the region. The source of
drinking water is ground water, and prior to the outbreak, chlorination was not part of the water treatment
process. Additional manure related infectious disease outbreaks have been reported by [Morgan et al.
(1998), Solomon et al. (2002)], and Gordeiko et al. (1990). Rather interestingly, two Q-Fever outbreaks
related to manure were reported: one in Germany [Reintjes et al. (2000)] and one in England [Jorm et al.
While the above summaries concern outbreaks of disease serious enough to involve the public health
authorities, other diseases, though less serious, are more common. It was estimated in 1998 that 2-4 million
persons were infected with some form of salmonella (USDA, 1994). Salmonellosis is characterized by flu-
like symptoms, possibly accompanied by nausea, vomiting, abdominal cramps and diarrhea. Except for
Salmonella typhi, which is exclusively a human disease, other forms of salmonellosis do not have high
mortality rates but do have high morbidity rates and are highly transmittable. Major foodborne outbreaks
have been related to consumption of beef, poultry, homemade ice cream, and pork (USDA, 1994). It may
also be present in eggs. The incidence of salmonellosis appears to be rising both within the U. S. and in
other industrialized nations. S. enteriditis isolations from humans have shown a dramatic rise in the past
decade, particularly in the northeast United States (6-fold or more).
4.2.5 Animal Diseases
While the common pathogens may be a risk to humans, they are also a risk to other animals. Wild
animals moving near manure application sites may carry diseases to new areas. Most ruminants, deer, elk,
and others will probably be sensitive to the same organisms that affect cattle. Poultry diseases may also
affect other birds. Geese and ducks are known to carry Cryptosporidium and Giardia.
Distribution of manure beyond the production facility bears the possibility of serious environmental
and economic consequences, such as, for example, if there is an asymptomatic carrier of a disease. The
manure from that farm could spread the disease to several other farms receiving manure as fertilizer. The
consequences could range from increased veterinary bills to treat affected animals to wholesale destruction
of infected animals, depending on the disease being spread. Biosecurity of farms has become an important
issue with the USDA publishing several guidelines for farms to help secure production facilities from
external contamination. Not all pathogens are present at every CAFO. Understanding the distribution of
pathogenic organisms makes it easier to design control strategies that will reduce risk. Table 4.3 shows the
sources of common zoonotic diseases on farms as a function of livestock species (Cole, 1999).
Reservoirs for Yersinia enterocolitica include most domestic mammals, particularly swine.
Reservoirs for Yersiniapseudotuberculosis include a wide variety of domestic mammals and fowl. The
recently discovered hemorrhagic colitis strains of Escherichia coli belonging to the O157:H7 serotype are
usually acquired after ingestion of either rare ground beef or raw milk. They have also been shown to be
transmitted via water. These verotoxin-producing (shigatoxin) strains have been isolated from calves and
pigs with enteric diseases and from retail pork and lamb. Reservoirs of Campylobacter jejuni include cattle,
sheep, swine, dogs, and domestic poultry (USEPA, 1998). Both E. coli O157:H7 and Salmonella spp. are
carried by ruminants, especially cattle, and at least one to five percent of cattle shed E. coli O157:H7 in
feces. (Altekruse et al., 1997; Hosek et al., 1997).
Table 4.3 Sources of common zoonotic diseases on farms.
The gram positive bacterium Listeria monocytogenes is widely distributed in the environment and is
associated with decaying vegetation, soil, sewage, and feces of animals. Many cases of human listeriosis
have been associated with consumption of fresh vegetables possibly contaminated with manure from
ruminant animals. L. monocytogenes may grow on a variety of vegetables even at refrigeration
temperatures. (Brackett, 1999) Therefore, the potential for introduction and transmission of L.
monocytogenes from manure and soil amended with raw or poorly treated manure on produce may be
greater than vegetables grown in soil amended with treated manure.
Antibiotics are used extensively in animal production. Approximately 2.5 million kilograms of
antibiotics per year are used on livestock in the United States (Kolpin et al., 2000). Of this amount, about
10% is used to treat active infections while the remaining nearly 90% is used for growth promotion and
Antibiotics may be beneficial in agriculture, but there are growing concerns about the effects of
antibiotics in the environment, especially the possibility of the increase in populations of drug-resistant
microbes. An increase in drug resistant microbes could make it more difficult to treat diseases in animals
and humans. Almost 50% of the antimicrobial agents in North America are used by agriculture. The
majority of agricultural use is for growth promotion in farm animals. Growth promotion uses low doses of
antibiotics that may lead to more bacterial resistance than higher doses used therapeutically (McGreer,
Antibiotic residue may be found in animal by-products (manure and urine). This waste may
come in contact with humans, other animals, and surface and sub-surface waters through run-off and
leaching. The concentrated use of antibiotics at CAFOs makes it more likely to have antibiotic residue and
antibiotic resistant microbes in the vicinity.
Wide use of antibiotics may lead to development of resistance among the microorganisms that the
antibiotics are being used to control. Antibiotic resistance develops in microbial populations due to the
selective pressure exerted on the population by the antibiotic. If the level of antibiotic used is inadequate to
completely eliminate the microorganisms from the animals some members of the population will survive.
These organisms will continue to increase their resistance to the antibiotic until the antibiotics are no longer
effective in controlling populations or diseases. The enzymatic capacity for resistance to antibiotics may be
transferred in the environment by different mechanisms. Plasmids may be transferred directly from
microorganism to microorganism, by bacteriophages, or upon cell lysis, leading to the uptake of free
plasmids by other organisms. Increasing microbial resistance to antibiotics raises the possibility of hard-to-
control animal sickness and require use of multiple antibiotics for treatment. Microbes could then become
resistant to multiple antibiotics. Since the antibiotics may also be spread throughout the environment via
manure and urine, other microbes that come into contact may also become resistant. This includes not only
microbes that lead to animal diseases but to human maladies as well. Since the antibiotics used for animals
are often the same for humans, different antibiotics may have to be used to fight the resistant microbes. One
possibility to prevent this particular problem would be to limit the use of "human" antibiotics on animals.
4.3.1 Case studies on the effect of antibiotics related to CAFOs on the environment:
188.8.131.52 Case 1 - Chesapeake Bay
In the Chesapeake Bay area, manure from a chicken CAFO was used to fertilize fields. The runoff
from these fields fed into the Pocomoke River changing the ecology of the river. Recently an outbreak of
Pfiesteriapiscicida, which is toxic to fish and human health, was attributed to the influx of antibiotics from
the field runoff. A study has shown that this strain of Pfiesteriapiscicida found in the Pocomoke River is
antibiotic resistant whereas other strains from similar rivers do not show the same antibiotic resistances
(Isbister et al., 2000).
184.108.40.206 Case 2 - Iowa Swine Operations
A study conducted by the Iowa Department of Public Health on the effects of CAFOs on the
environment showed the presence of antibiotics and antibiotic-resistant microbes in the earthen manure
lagoons. The tests revealed an antibiotic in an earthen manure lagoon monitoring well. Four different
antibiotics (tetracyclines, sulfonamides, p-lactams, and macrolides) were found in detectable concentrations
Table 4.4. Antibiotic Levels in the Lagoons and one Monitoring Well (adapted from Table 7) (Iowa Dept. Public Health, 1998)
Collection Sites (Farm)
Monitoring Well (8)
E. coli, Enteroccus, and, Salmonella were obtained from the lagoons, wells, and drainage ditches on
the sites. All these microbes showed varying antibiotic resistance (Iowa Dept. Public Health, 1998).
220.127.116.11 Case 3 - Shoal Creek
Researchers studying bacteria in Shoal Creek, located in Barry County, Missouri, found detectable
concentrations of antibiotics in the creek. This northwest section of the county produces 33 million broiler
chickens and 300,000 turkeys annually. The antibiotic source was found to be a chicken CAFO located
upstream from where the antibiotics were found. Antibiotics used to treat both animals and humans as well
as human only (located downstream of sewage plant effluents) were also found. Further study on the impact
of the antibiotics to the watershed and ecological structure of Shoal Creek is on-going (Penprase, 2001).
18.104.22.168 Case 4 - A National Reconnaissance
The U.S. Geological Survey tested water samples from 139 streams in 30 states in 1999 and 2000.
The selection of sampling sites was biased toward streams susceptible to contamination (i.e., downstream of
intense urbanization and livestock production). The samples were tested for pharmaceuticals, hormones,
and other organic wastewater contaminants. Of the 95 organic wastewater contaminants tested,
approximately 20 antibiotics were measured and only eight were not found in the samples (however, some
of them may have been present in the stream sediment due to "their apparent affinity for sorption to
Figure 4.3 shows the frequency of detection and percent of total measured concentration for the
contaminants, by category (Kolpin, et al. 2002).
The widespread use of antibiotics in agriculture, especially CAFOs, is now becoming an area of
investigation in the United States.
4.4 Endocrine Disrupting Chemicals Associated with Concentrated Animal Feeding Operations
Endocrine disrupters are a class of chemicals of growing interest to the environmental community.
The U.S. Environmental Protection Agency's (EPA) Risk Assessment Forum defined an endocrine
disrupting chemical (EDC) as "an exogenous agent that interferes with the synthesis, secretion, transport,
binding, action, or elimination of natural hormones in the body that are responsible for the maintenance of
homeostasis, reproduction, development and/or behavior (EPA 1997) ". Most of us are more familiar with
chemicals of concern that have a specific health outcome such as lung cancer. However, EDCs are a class
of chemicals defined by their mode of action and may result in a variety of health outcomes. For example,
an EDC may initiate a health-related outcome in humans or wildlife by binding to and stimulating estrogen
or androgen receptors.
Steroid hormones are chemicals of concern to endocrine health associated with CAFOs. Steroid
hormones are used by many animals to facilitate the control of their body systems. Mammals, birds,
reptiles, and fish produce virtually the same steroid hormones and possess receptors that bind the steroids to
receive their control messages (McLachlan 2001). In this section, the term hormones will refer to steroid
hormones. Until risk assessments are completed, it is assumed that all endocrine active compounds that
have the potential to interact with the environment are chemicals of concern. Thus, the chemicals of
concern are those hormones naturally produced and excreted by animals and those hormones administered
to animals as drugs and are excreted. These animals remove hormones from their bodies by excreting them
Figure 4.3. Frequency of detection of organic wastewater contaminants by general use category (4A), and percent of total
measured concentration of organic wastewater contaminants by general use category (4B). Number of compounds in each
category shown above bar (Kolpin, et al., 2002).
in urine or feces. Many of the methods of storage, treatment, and disposal of animal wastes at CAFOs allow
contact of the waste with the environment. Since many animal species respond to the same hormones, it
may be possible to disrupt the natural state of the endocrine systems in wildlife exposed to waste from
CAFOs. If CAFO-generated hormones are transported to water bodies (surface or ground water), exposure
to humans may be possible.
The classes of natural (biogenic) hormones that may be excreted by animals include estrogens,
androgen, progesterones, and thyroid hormones. Although ideally all hormones would be considered in this
risk management evaluation, there is almost no information available about natural hormones and animal
feeding operations other than estrogens and, to a lesser extent, androgens. There is no information available
on CAFOS and thyroid hormones. Thus, the focus of this section will be on natural estrogens and
The chemical structures of the primary natural estrogens are shown in Figure 4.4. Here, they are
shown in their biologically-active forms. Generally, hormones the body wishes to excrete are conjugated
with glucoronides or sulfonides. Conjugation eliminates their biological activity and increases their
solubility in water. Most literature concludes that excreted, conjugated hormones are deconjugated
relatively quickly in the environment by enzymes produced by common bacteria
(Schiffer, Daxenberger et al. 2001). It will be assumed that hormones in contact with the environment are
not conjugated. The most active estrogen is 1?P estradiol, while estrone and estriol are metabolites of
estradiol with much less biological activity.
Figure 4.4. Structure of biogenic hormones.
4.4.1 Xenobiotic Hormones
The U.S. Food and Drug Administration (FDA) has approved the veterinary use of the six hormones
(Table 1) and only for cattle and sheep (21 CFR, Chapter 1, Part 522). Patented forms of the natural
hormones are often used in cattle and sheep production. These include estradiol benzoate (l?p-estradiol 3-
benzoate) and estradiol valerate (l?p-estradiol 17-pentanoate), testosterone propionate, and various
derivatives of progesterone, genetically called progestins. Xenobiotic hormones administered to cattle and
sheep include trenbolone acetate (TbA), melengestrol acetate (MGA), and zeranol. Zeranol is an estrogen
mimic. TbA is hydrolyzed in vivo to the biologically active chemical, trenbolone-1?P (TbOH-l?P)
(Schiffer, Daxenberger et al. 2001). TbOH-l?P acts as an androgen, and an antiglucocorticoid. TbOH -1?P
Figure 4.5. Chemical structure of Trenbolone acetate and hydroxide.
may be metabolized to TbOH-17ae which is 40 times less active than TbOH- l?p. Zeranol is an estrogen
mimic. The chemical structures of these compounds are shown in Figure 4.5.
MGA is used for estrus synchronization or induction to improve feed efficiency and weight gain in
heifers (Schiffer, Daxenberger et al. 2001). MGA acts as a progesterone and glucocorticoid.
The parent veterinary drug, trenbelone acetate (TbA), is metabolized to the biologically active
chemical, trenbelone-l?P (TbOH-l?P) and TbOH-17a. The P and a are isomers where the methyl and
hydroxyl groups are cis and trans, respectively.
Since steroid hormones are the signal molecules of the endocrine system, organisms exposed to
these hormones have the potential for adverse endocrine related effects. The consequences of excess
estrogen in humans may be dramatic (Williams Textbook, 1998) and effects at low doses are possible
(Anderson, 1999). Unintentional exposure of wildlife to estrogens has focused mostly on fish: vitellogenin
production in male fish has been observed when exposed as little as 1 ng/1 1?P estradiol or 25 ng/1 estrone
(Routledge, 1998). Other estrogen-related health effects observed in wildlife include abnormalities in
reproductive organ development and sex change. In vitro assays that measure binding to human steroid
receptors have shown that TbOH -1?P binds to the human androgen receptor as strongly as the natural
human androgen, dihydrotestosterone, and MGA binds 3.5-times stronger to the human progesterone
receptor than progesterone itself (Bauer, Daxenberger et al. 2000).
4.4.2 Uses of Hormones in CAFOs
Farm animals generate, use, metabolize, and excrete natural hormones, the type and quantity
depending on the animal, sex, and reproductive state.
The FDA has approved the veterinary use for cattle of the hormones listed in Table 4.5 in single
hormone or dual hormone doses (21 CFR, Chapter 1, Part 522). The delivery of the hormones is typically
Table 4.5. Hormones Approved for Veterinary Use in Cattle
accomplished by ear implant (although delivery of MGA in feed is approved by the FDA). The FDA has
approved several dual hormone implants, including an implant containing 20 mg TbA and an implant
containing 20 mg estradiol benzoate with 200 mg testosterone propionate. Data on the rate of use of these
hormones in the United States were not found.
Arcand-Hoy et al. (Arcand-Hoy, Nimrod et al. 1998) estimated the use of exogenous estradiol
(presumably the sum of the use of simple estradiol and the benzoate and valerate forms) to farm animals to
be 580 kg/yr in the United States.
4.4.3 Release of Hormones to the Environment
Since hormones are present in animal excreted waste and in their bodies, excreted waste (urine and
feces) and animal carcasses that come into contact with the environment must be considered as likely
sources of hormones to the environment. Although the hormone content of waste has not been
systematically studied, a relatively large total mass of hormones is released yearly given the estimated 291
billion pounds of manure generated annually in the United States (EPA 2001). The avenues of release of
animal waste into the environment at CAFOs are described in detail in other sections of this RME. These
releases may be associated with leakage from storage lagoons, runoff from composting operations, land
application of waste, and other scenarios. There are very little data to quantify the release rates of hormones
to the environment from CAFOs. One study found that chicken litter may contain > 100|ig/kg estrogen and
that runoff from a field receiving poultry waste contained up to 3.5 |_ig/l estradiol
(Shore, Cornell et al. 1995). A similar study found 1.3 |ig/l estradiol in runoff from land applied with
poultry waste (litter) (Nichols, Daniel et al. 1997). Testosterone was found in rooster litter up to 670 |ig/kg
(Shore, Harel-Markowitz et al. 1993). In another study, MGA and metabolites of TbA were measured in the
dung of cattle given implants of MGA or TbA (Schiffer, Daxenberger et al. 2001). The maximum levels
found in the dung were 7.8, 75, 4.3 |ig/kg of MGA, TbOH-17a, and TbOH -170, respectively. Although
there is little data, the U.S. EPA acknowledges that hormones should be considered in assessing the
environmental impact of CAFOs (EPA 2001).
A recent news article quoted as yet unpublished work by U.S. EPA and university researchers
regarding a study of the hormonal character of a stream associated with a cattle feedlot in Nebraska (Raloff,
2002). The research found that water collected downstream of the feedlot had significantly higher
androgenic activity than water collected upstream.
4.5.1 Use of Metals in Animal Feed
Animals in CAFOS produce a great amount of manure that is applied to land as fertilizer. The metal
content of animal waste is in question. Metals are being supplied to farm animals via diet. This review of
the literature investigates the disbursement of the nutrient-rich excreta and the effects that are or may be
Metals in discussion here are copper, zinc and arsenic. While trace amounts of some elements are
necessary for life, quantities above and beyond those amounts are fed to swine and poultry as growth
promoters. Usually arsenic (often in the form of "roxarsone", Christen, 2001) is fed to chickens for this
purpose, even though arsenic is not a required nutrient; exaggerated amounts of copper and zinc (often in
the form of CuSC>4 and ZnO or ZnSC>4, respectively) are typically used in the swine diets. Possible adverse
effects reported in the literature include the risk of phytotoxicity, groundwater contamination, and
deposition in river sediment that may eventually release to pollute the water, the effect of manure
application on grazing animals and also the result of using chicken litter for livestock feed.
The use of excess metals to promote growth is practiced in many countries. For example, Canada (
DeLange, 1997), Great Britain (Nicholson, 1999), Japan (Eneji, 2001), France (Martinez, 2000), Germany
(Rothe, 1994), Spain (Alonzo, 2000), Denmark (Tom-Petersen, 2001) and others have engaged in research
to address issues similar to those of concern in the United States. Though the study parameters and
methods of research may differ, overall, there are questions and conclusions that are nevertheless relevant to
the demands of this discussion and are therefore taken into consideration.
The following table (Table 4.6) presents dietary/manure content data to give the reader an idea of the
amounts of copper and zinc consumed by pigs when fed diets that achieve normal growth and those that
promote growth. Arsenic is not a dietary requirement for poultry, the growth promoting level 5-10 ppm
yields manure with 15-45 ppm (Muller, 2002; Chaney, 2002; Alonso, 2000; Ohio State Univ Bulletin,
Table 4.6 Copper and zinc in swine diets
Swine Diets (ppm)
4.5.2 Mobility of metals in soil
Mobility of the excreted metals has been addressed by some sources. Martinez (2000) examined the
copper and zinc balances in soil after five years of repeated pig slurry applications. The results showed that
most of the nutrient copper and zinc (80% of what was applied) remains in the top 0-20 cm of the soil layer.
Tables 4.7 and 4.8 show soil analysis data for copper and zinc.
Table 4.7 Soil Cu balance after five years of repeated pig slurry application.
1 1"? ^
Table 4.8 Soil Zn balance after five years of repeated pig slurry application.
91 1 £
Gettier et al., (1988) is in agreement by finding that copper, when applied to the soil surface via pig
manure, shows little movement through the soil profile (i.e., 0-20 cm) used in that experiment. (Also, see
Table 4, data from World Animal Science, 1987.) It was reported that copper applied to soil generally
results in a linear increase in extractable copper. Similarly, Mohanna et al., (1999) found a linear
relationship between dietary zinc supplementation and the amount excreted. It has been advised that, with
pig slurry application, immediate effects may not be recognized. Because metals may accumulate in the
topsoil, it may be the longer term applications that reveal adverse effects (i.e., changes in soil biomass and
herbage metal concentration) (Christie et al., 1989 and Eneji et al., 2001).
During an eight year period, Martinez et al. (2000), assessed the copper and zinc content of soil and
drainage water in soil subjected to intensive pig slurry application. About 62% of the applied copper and
74% of the applied zinc remained in the soil as EDTA extractable forms. Only 0.05% and 0.6%,
respectively, were present in the drainage water. A study of 18 soils in the Netherlands reported
information concerning the correlation of organic matter and desorption of several metals (Impellitteri, et
al., 2002). The results indicated that increasing pH increased soluble organic matter and Cu. Increased Ca
flocculated organic matter and restrained Cu in solution. McBride (1994) stated that Cu added to soil will
remain there for very long times. High organic matter increases mobility, but Cu is least soluble at pH near
seven. Zinc may leach to lower levels of the soil if there are significant inputs of Ca to displace it from the
exchange sites. Arsenic behaves in soil much like phosphate. That is, As only moves lower in the soil
profile if the sorption capacity of the upper layers is filled. Based on this information, the amount of metals
in the drainage may be very small, but some of the excreted metals do get carried into the groundwater,
eventually making their way to a stream or river bed. Here, strewn about the sediment, the metals may be
set into motion again as environmental conditions change (e.g., pH, redox potential, or high stream flow)
(Lim et al., 1995). At that point, environmental consequences may become severe, even if they are delayed
in time from the point of initial contamination. As, Cu, and Zn all have potential toxicity to plants and
animals. Arsenic is found in soils from about 3.6 to 8.8 mg/kg. Copper is found in soils from about 14 to
29 mg/kg. And zinc is found in soils from about 34 to 84 mg/kg. Copper and zinc are both essential
elements for plant and animal life. The needed levels and the toxic levels will change as environmental
conditions change. Arsenic is not an essential element and is more toxic to plants and animals than Cu or
4.5.3 Metals in plants
Christie et al. (1989), conducted a sixteen year study addressing herbage concentrations of copper
and zinc that had reached 10 and 44 mg/kg, respectively. The purpose was to determine the toxicity to
grazing sheep. See Table 4.9 for content data. While a very high rate of application (200 m3/ha/yr) was used
to test extreme conditions, this rate produced enough soil copper and zinc accumulation sufficient to
produce a toxic response from sheep (>10 mg/kg). Sheep are especially susceptible to excess copper, and a
prolonged ingestion of just 15-20 ppm of copper may result in the occurrence of fatal hemolytic crisis.
(World Animal Science. 1987)
Table 4.9 Cu and Zn in soil (top 5 cm), February, 1987 and herbage first cut of 1986.
All values are mg/kg dry material. L.S.D. least significant difference (minimum difference to have significance).
While some studies proposed a threat of copper and zinc phytotoxicity, there was not an abundance
of conclusive data. Tom-Petersen, 2001, explained that if the accumulation of copper in the soil reaches a
toxic level, structure and function of the microbial community may be affected. But this source goes on to
say that a lack of knowledge on the interaction between copper and the biota makes it difficult to assess the
impact on a biological system. Likewise, Gettier, et al., 1988 states that while a high level of copper in soil
is phytotoxic, the amount of copper that may may safely be added to a soil system has not been well
defined. World Animal Science, 1987, has indicated that zinc is partly added to high copper diets to
counteract the accumulation of copper in animal tissue, and accumulation of either of these metals in soil
could cause phytotoxicity in which the plant root system is affected first.
4.5.4 Metals in Animals
Alonso, et al., 2000, performed a study to determine whether pig slurry treated fields have an effect
on the accumulation of copper and zinc in grazing cattle. It has been suggested that ruminants may be more
at risk for copper toxicity because of their efficiency in absorbing trace elements across the gut, which may
lead to toxic levels of copper in the liver. When the liver reaches saturation with copper, the copper is
released quickly into the blood. In sheep, copper may cause fatal hemolytic crisis. This study concluded
that, in areas with the highest pig densities, more than 20% of the cattle examined had hepatic copper levels
exceeding the toxic concentration of 150 mg/kg fresh weight. Zinc liver levels, however, did not seem to be
of any consequence.
The use of chicken litter (consisting of poultry manure, feathers, bedding, and spilled feed (Poore, et
al., 1998) as livestock feed is yet another area of concern. While broiler litter has been used for over fifty
years with no major problems, research performed at Virginia Tech. reported increases in arsenic and
copper concentrations in the livers of cattle fed poultry litter. The arsenic concentration, however, returns to
control levels within three days of withdrawal. Therefore, most states recommend a fifteen-day withdrawal
period prior to slaughter. A related study indicated that while increased liver copper concentrations in cattle
fed poultry litter without adverse effects have been reported, it was found in this study that the feeding of
1.13 kg CuSO/t/90.7 kg chicken litter to cattle resulted in chronic copper toxicosis. However, this condition
may be reduced by supplementation of molybdenum and thiosulfate (Banton, et al., 1987). For reference,
the level of arsenic in a typical chicken manure/litter is about 25 ppm. (Chaney, et al., 2000) A literature
search for additional information regarding the role of arsenic contamination of soil via chicken manure
(e.g., phytotoxicity, drainage water, sediment residue, etc.) was not fruitful.
Metals are excreted in various forms by animals. A common form of copper is the divalent ion that
may form complexes with organic matter. Similarly, zinc has a divalent form that will also complex with
organic matter. Arsenic more closely resembles phosphorus in its behavior.
The following comments are extracted from this review of dietary copper, zinc, and arsenic
consumption by pigs and poultry and the distribution of these metals when excreted.
1. Copper and zinc are fed to swine in concentrations that exceed the minimum requirements to induce
a growth promoting effect. In chickens, arsenic is used as a supplement for growth promotion;
arsenic is not a dietary requirement in chicken feed.
2. Approximately 80-90% of the copper, zinc, and arsenic consumed is excreted.
3. Most of the excreted metals, contained in manure/slurry for land application, settle in the topsoil,
approximately the first 0 - 20 cm of soil.
4. World Animal Science, 1987, reports that pig manure slurry, on the average, contains six times
more copper than either poultry or cattle slurry. This presents a more striking danger of copper
enrichment in those soils being fertilized with pig excreta.
5. Zinc added to a high copper diet helps thwart the possibility of copper toxicity.
6. In swine, the response to feed additives is greatest in starter diets (10-50 pounds). Higher levels of
copper and zinc are typically found in the diet at this level. (KSU, October 1997)
7. A management plan needs to be established for each CAFO, on an individual basis, that takes into
account variables such as soil type, soil pH, land area for manure application, level of waste water
produced, animal density, anticipated metal output, etc.
8. There is a need to identify other growth promoters that would be non-toxic, or at least identify other
forms of the metal compounds being used now that would be more bioavailable. For example,
cupric citrate was found to promote growth at lower levels than cupric sulfate pentahydrate, resulting
in less litter copper (Pesti, et al., 1996).
5 STRESSOR TRANSPORT
In the large quantities present at CAFOs, animal manure contains enough watershed stressors to be a
significant source of environmental pollution. This section describes the ways in which the stressors in
manure may be released into the environment. Overland transport in wet weather flow, subsurface transport
to and through groundwater, and airborne transport and deposition are the primary pathways by which the
environmental stressors in animal manure reach the environment. Understanding these pathways is
important in developing strategies for managing the environmental risk posed by animal manure.
This section of the RME describes overland transport in wet weather flow, subsurface transport, air
transport, and deposition in that order.
5.1 Transport Mechanisms
5.1.1 Overland Transport in Wet Weather Flow
The impact of wet weather flow and sediments from confined animal feeding operations (CAFOs)
could be significant to maintaining a watershed environmental quality. Wet weather flow may provide
conditions that result in the transport of contaminants and sediments to a receiving water. Sediment may
prove a significant stressor to a watershed as sediment itself or as a medium for the transport of other
stressors such as nutrients, pathogens, or chemical stressors. The processes responsible for the generation,
transport, and deposition of sediment into a receiving water are primarily erosion, overland flow, and
deposition. The effects of these physical and chemical processes will be dependent on the type of CAFO
and the operations of facilities and their waste handling strategies. This section outlines some of the
principal physical and chemical processes affecting sediment impacts from CAFOs, how these processes
impact typical CAFO operations, and to identify areas of research as related to the reduction of sediment
impacts on watersheds from CAFOs.
5.1.2 Physical and Chemical Processes Affecting Sediment Impacts
Three primary components of runoff are overland flow or surface runoff, interflow and groundwater
flow. Overland flow is the portion of precipitation that flows over the ground surface until reaching a
receiving point, such as a channel, stream, or pond. Overland flow occurs typically after the infiltration
capacity of the soil has been exceeded. Interflow, also referred to as sub-surface storm flow, is the portion
of precipitation that travels just under the soil surface until it reaches a receiving point. Groundwater flow,
also referred to as baseflow or dry-weather flow, is the portion of precipitation that infiltrates the soil and
percolates deeper until reaching the water table, and later potentially emerging as a component of stream
flow downgradient from the infiltration zone.
5.1.3 Overland Flow
When precipitation first reaches the ground surface, it begins to infiltrate the soil. The rate of
infiltration, called the infiltration capacity, decreases over time. This decrease is primarily due to the
saturation of the soil void volumes. Once the soil becomes saturated, infiltration continues at an
approximately constant rate, assuming that the precipitation event continues at an intensity equal to or
greater than the infiltration capacity. In general, the infiltration rate for clayey soils is less than that for
If the intensity and duration of precipitation is great enough to exceed the infiltration capacity of the
soil, water will begin flowing over the ground surface as surface runoff. Some of this runoff flows into
small puddles and ponds, and is termed depression storage. Runoff retained in depression storage may
experience further infiltration or if the capacity of the depression is exceeded, overland flow will continue
either until another depression, a stream, or receiving water body is encountered.
The wide variability in soil type, topography and vegetative cover within a watershed, coupled with
the inconsistency of precipitation, results in some areas contributing a larger portion of runoff to stream
flow and other areas contributing much less or not at all. The partial area contribution concept has been
used to describe this behavior and it has been noted that in some watersheds as little as 1-3 % of the total
basin contributes overland runoff to stream flow.
The portion of infiltrated water that travels under the soil surface toward a receiving water body is
interflow or sub-surface storm flow, and the movement of interflow is much slower than overland flow.
This component of runoff is typically important in areas with permeable soil overlying less permeable soils
or sub-surface materials, such as bedrock or clay, as may be the case of farm fields that are plowed and have
a high percentage of organic material incorporated into the soil structure.
In many watersheds, the concept of variable source area contribution is important or dominates
runoff closer to stream channels or receiving water bodies with shallow water tables, or where shallow
impervious materials underlie the surficial soils. A variable source area in general is an area that expands or
contracts depending on the precipitation event and initial soil moisture conditions, and occurs when soils
become saturated from below due to a rising water table. As precipitation continues, the soils become
saturated by the rising water table which in turn expands the area over which runoff will occur.
5.1.5 Groundwater flow
Groundwater flow, also referred to as baseflow or dry-weather flow may account for a substantial
percentage of subsurface runoff from a watershed or to a receiving water body. Precipitation that continues
to infiltrate the soil surface after the soil is saturated, and does not become interflow, percolates downward
by capillary action and gravity until reaching the water table or an impermeable geologic unit. The area
within a watershed, where infiltrating precipitation eventually reaches the water table and becomes
groundwater, is termed a recharge area. Groundwater flows from areas of high potential (recharge area) to
areas of low potential (discharge area). Recharge areas are typically topographically higher in elevation
than discharge areas that are usually incidental with a stream, river, or pond.
5.2 How These Processes Impact Typical CAFO Operations
Runoff, and the various components of runoff have varying degrees of importance in the context of
CAFOs. The area of consideration at the individual CAFO is important when determining if runoff may be
a concern. Runoff may occur from several areas, including the roof of a barn or other type of shelter used to
house animals, external feeding areas that may or may not be paved, and may or may not be diverted to a
lagoon or holding pond, pasture lands used for animal grazing, and crop lands that receive animal waste as a
In this discussion, water that is used to flush animal waste generated inside a barn or shelter to a
holding facility is not considered part of runoff. If this material is incorporated into the soil surrounding the
CAFO, the materials in this water, both physical and chemical, will be susceptible to runoff processes.
Runoff may or may not have any associated impact or concerns. Depending on the flow path and
material encountered during the generation of runoff, water has the ability to pick up physical and chemical
components that may degrade the receiving waters. These potentially degrading compounds include
sediments, nutrients, pathogens, EDCs, heavy metals, and pesticides. These various compounds are
discussed in separate sections. Additionally, runoff has the ability to cause flooding.
Many conditions contribute to the generation of runoff including topography, geology, soil type and
thickness, precipitation intensity, duration and form (rain versus snow), vegetative cover, climate and
season, soil moisture, evapotranspiration, depth to groundwater, presence of vegetative buffers, condition of
the land surface (recently plowed and plowing technique) and size of the field, farm or watershed in
5.2.1 Suspended Solids and Sediments (SSAS)
SSAS production from CAFOs may be attributed to three primary sources; direct erosion, loss of
impoundment/lagoon sediments, and waste handling/disposal processes. Direct erosion may be an obvious
source of sediment in certain CAFOs, such as beef cattle feedlots, dairy operations, or other outdoor
operations. Erosion from these operations will be subject to erosion processes typical of other agricultural
practices. SSAS from impoundments/lagoons may be controlled by the design of the impoundment/lagoon.
Waste handling/disposal processes may also generate SSAS. For example, land application is typically used
for swine waste. Though the waste will have undergone some preliminary settling during handling and
storage, the application of the waste to agricultural fields may result in particles being applied to the field, as
well as, the waste adhering to the SSAS generated from the erosion of the agricultural soils.
The natural processes of erosion results in a background sediment load to receiving waters. Erosion
is the term used for the gradual wearing away of the earth's surface due to natural physical and chemical
processes. Millar et al.,(1965), differentiates between geologic and soil erosion. Geologic erosion is
defined as the erosion of the earth's surface under natural conditions when the land surface and the
vegetative cover are undisturbed. Geologic erosion is a relatively slow process and natural in-stream
processes are typically able to assimilate the sediment loadings that result. Soil erosion is defined as the
unnatural erosion of the land surface, typically due to man's activities such as deforestation, tilling, or other
activities. The natural processes of erosion may be significantly accelerated by man's activities. Research
has been conducted on conditions and practices that affect soil erosion such as soil properties, the impact of
typical agricultural practices, deforestation, and burning (Braskerud, 2001; Butler and Karunaratne, 1995;
Carpenter et al., 2001; Haigh and Gentcheva-Kostadinova, 2002; Kondolf et al.,In Press; Lau et al., 2001;
Lisle et al., 1998; Martin-Vide et al., 1999; Midmore et al., 1996; Millar et al., 1965; Nash and Halliwell,
2000; Peterson 1999; Uri and Lewis, 1998; van der Werf and Petit In Press; and Woo et al., 1997). This
research has focused on retaining topsoil and soil structure for maintaining or enhancing agricultural
production. The impact of CAFOs with respect to SSAS has not been thoroughly considered.
In this document, erosion will be limited to that caused by water. Erosion by water is typically
divided into four categories: splash, sheet, rill, and gully erosion. Splash erosion is the deterioration of the
soil structure due to the impact of a raindrop onto the soil surface. The impact breaks down the soil
structure and the water from the droplet carries away or erodes some of the soil. Sheet erosion is erosion
typically over a smooth, lightly sloped soil and results from overland flow. This results in a gradual uniform
removal of soil particles. However, sheet erosion seldom occurs without forming rill erosion. Rill erosion
is the result of pockets of water forming in small depressions. The water leaving these pockets form small
rivulets of flow, which erode small channels into the soil. The small channels cut are called rills. Sheet and
rill erosion are typically due to overland flow. Left unchecked, the small channels enlarge to form larger
channels that eventually combine to form still larger channels. As these channels increase in size their water
carrying capacity increases, which consequently results in a greater capacity to erode the soil. Once these
channels work down through the soil structure, they form what is known as gully erosion. Gully erosion is
the combined process of waterfall erosion, channel erosion, and freeze/thaw erosion. Gully erosion is easily
identified and typically indicates severe neglect. This form of erosion may significantly add to the sediment
load of a nearby receiving water.
Erosion generates the particles that are carried to the receiving water to become suspended solids
and sediment. Once in the receiving water, in-stream processes control whether the SSAS are deposited or
carried downstream to be deposited later. These in-stream processes are beyond the scope of this work and
for the most part are not necessary to the issue of managing SSAS from CAFOs.
5.2.2 Stress due to SSAS
SSAS may act as a stressor directly on an aquatic system or indirectly by transporting particle bound
stressors. As a direct stressor, SSAS may significantly increase the turbidity in receiving water. This
increased turbidity may dramatically reduce the primary production of the water column by limiting the
light penetration (USEPA, 2001b). Depending on the physical and chemical characteristics of the SSAS,
the turbidity may persist downstream even with significant dilution and/or settling time. SSAS may also
result in siltation of a receiving water. Siltation may result in a loss of critical habitat, loss of water carrying
capacity, and increased need for dredging or other waterway maintenance.
SSAS may also serve as a significant source of particle bound stressors. Contaminants that are
particle bound may increase the aquatic exposure in the receiving water by renewed exposure through
resuspension and redeposition. These particle-bound contaminants may include nutrients, pathogens,
metals, and organic contaminants. Nutrients such as nitrogen, phosphorus, and potassium may be carried by
SSAS to a receiving water. CAFO wastes are typically high in these components (USEPA, 200la) and
depending on the chemical form of the nutrient, the SSAS may serve to transport these stressors. Pathogens
are also found in CAFO wastes and may be associated with soil particles and sediments. The interactions
between pathogens and SSAS are beyond the scope of this report. In addition, organic contaminants (such
as EDCs, antibiotics, etc) trace metals, and salts may be associated with SSAS. These stressors are
addressed in other sections of this document.
SSAS may also act as a stressor by reducing the available dissolved oxygen in a receiving water.
The organic content of CAFO waste is animal specific. In general, beef/dairy waste has a high organic
content in the form of undigested cellulose. Swine waste and poultry waste are lower in organic content.
The organic content is important as it provides an organic substrate for microbial activity. This microbial
activity uses available dissolved oxygen in the water column. If the oxygen demand exceeds the available
dissolved oxygen (DO) and the rate of re-aeration, the DO may drop to levels that are critical for
maintaining a viable ecosystem. The oxygen demand is commonly measured as either a biochemical
oxygen demand (BOD), which is the oxygen demand required to biologically stabilize the biodegradable
components, or a chemical oxygen demand (COD), which is the oxygen demand needed to chemically
oxidize organic and inorganic components regardless of their biodegradability (Millar et al., 1965). With
all the considerations of efficient management of SSAS and other stressors, economic design constraints
must be considered in the optimization of the design. The management strategies may not be so cost
prohibitive that the CAFO operator cannot afford the management. In the economic considerations, the
design should account for the impact on production, as well. For example, the design cannot be for a ten
acre detention basin on a five acre CAFO.
CAFOs offer a challenge to manage their impact on the environment and the economic production of
the animal product. However, the concentrated nature of their design offers an opportunity to engineer an
efficient and economic management solution and in the end potentially to reduce the overall waste load to
the environment from animal production whether confined or traditional.
5.3 Groundwater Transport
5.3.1 Statement of Problem
Storage and handling of animal waste in CAFOs and related agricultural practices are contributing to
groundwater contamination, and may have severe impact on surface water quality, since 40 percent of the
average stream flow is derived from ground water discharge as base flow (U.S.EPA 1993b in EPA-821-R-
01-003). Dairy operations were identified as the major source of groundwater contamination by nitrate in
excess of the MCL in the Chino Basin, California (U.S. EPA, 1998, Aton et al., 1988). This presents
potentially widespread impacts, since water from the Chino Basin is used to recharge the primary source of
drinking water for residents of heavily populated Orange County. In southeastern Delaware and the Eastern
shore of Maryland, over 20% of wells were found to have nitrate levels exceeding the MCL (U.S. EPA,
1998, Ritter et. al., 1989). Measured nitrate levels in ground water beneath Delaware poultry houses have
been as high as 100 mg/1 (Ritter et. al., 1989). Fractured aquifers (e.g., karst terrains developed in carbonate
rocks) underlie extensive, important agricultural areas in the eastern half of the United States (from Iowa, to
New Mexico and Texas, to Florida and Puerto Rico, and to Pennsylvania and New York) are particularly
vulnerable to nitrate by preferential transport (LeGrand and Stringfield, 1973). Evidence indicates that
leachate from lagoons located in well-drained soils (e.g., loamy sand) may severely impact groundwater
quality (EPA-821-R-01-003, Ritter and Chirnside, 1990), and that the use of manure in agriculture may
cause bacterial contamination in karst aquifers (Boyer, 1999). Since rural areas in the nation generally rely
on ground water as a drinking water source, they are at greater risk of nitrate poisoning than those drawing
from public water supplies (U.S.EPA, 1998, Nolan and Ruddy, 1996). Nutrients, pathogens, salts, toxic
metals, antibiotics, and hormones derived or excreted from animal waste and carcasses have the potential
for groundwater contamination and thus may cause an environmental problem. Nitrate and pathogens in
ground water impact human and animal health, and leaching salts may cause underlying groundwater to be
unsuitable for human consumption (U.S.EPA, 1998).
The cited case studies in California, Delaware, and Maryland are examples of nationwide problems
of subsurface water and groundwater contamination by confined animal operations and related agriculture,
including others in the Midwest. They underscore the importance of managing animal feeding operations to
minimize impacts on water quality and public health. The effectiveness of practices to control contaminant
losses from animal waste storage facilities and farmlands treated with animal manure depends, among other
factors, on the type of contaminants and their likely pathways in the subsurface and ground water.
Considerable scientific advances have been achieved in testing, measuring, and modeling the behavior and
fate and transport of pollutants in the environment in general, and in the subsurface in particular. However,
research is needed to further develop scientifically sound methods for assessing and managing the impact of
CAFOs on ground water. With the adoption of the Watershed Protection approach (WPA) as a strategy for
effectively protecting and restoring aquatic ecosystems and protecting human health (USEPA, 1995), risk-
based approaches for CAFOs are needed to better integrate environmental and socioeconomic factors in the
context of watershed management.
5.3.2 Pollutants, Sources, Transport, and Fate
Animal manure contains nutrients, particularly N and P, dissolved mineral salts, toxic metals,
microorganisms, and antibiotics. Among these constituents, however, nitrates, ammonia, and potentially
pathogenic organisms are the most common groundwater pollutants. They negatively impact human and
Efficacy of risk-based management of animal waste and manure-based agriculture requires
understanding the behavior of the pollutants in soil and the processes responsible for their transport through
the soil profile to ground water and surface waters. Figure 5.1 depicts potential pathways for movement of a
pollutant once introduced into soil. Areas with high soil permeability and shallow water tables are generally
most vulnerable to groundwater contamination by pollutants. Percolating water and lagoon leachate may
transport pollutants through the soil profile to ground water. Interflow (e.g., subsurface runoff and artificial
drainage) and ground water may deliver pollutants to surface waters through hydraulic connections. Not all
pollutants are susceptible to transport by leaching, because they are adsorbed onto soil particles, fixed
and/or transformed into organic forms by soil microbes. Mobility and persistence of pollutants are
controlled by physicochemical characteristics of the pollutant and the soil-aquifer system.
Processes responsible for transport and fate of major CAFO related groundwater pollutants are
discussed in the following sections in more detail only for nitrogen compounds, phosphorus, and pathogens.
Animal waste contains nitrogen in organic and inorganic forms, the latter of which is biologically
available to microorganisms and plants. Inorganic ammonia exists in two forms in natural waters:
ammonium ion (NH4+) and un-ionized ammonia (NH3). The un-ionized form is toxic to fish in low
concentrations. Whereas nitrate is water soluble and moves freely through most soils, ammonia compounds
are much less mobile and thus, much less susceptible to leaching in soils. Figure 5.2 depicts processes
primarily responsible for transformation of nitrogen compounds in sediments at the bottom of lagoons
(collection ponds) or in a topsoil layer treated with animal manure.
Ammonia due to direct loadings and to the decomposition of organic nitrogen (ammonification) is
oxidized under aerobic conditions in the process of nitrification to form nitrite (NCV) and then nitrate
(N(V). This process consumes oxygen and, thus, may seriously deplete the water body's oxygen levels.
Ammonia nitrogen may be lost by volatilization of un-ionized ammonia (NH3) from soil or a water body's
surface. Ammonium (NH4+) is biologically available for plant uptake.
Figure 5.1. Transport pathways of pollutants derived from animal waste.
Nitrate is water-soluble and moves freely through most soils. It is produced by nitrification of NH4+.
Nitrate is biologically available and may be taken up by plants. Under anaerobic conditions, nitrate may be
reduced to N2 by denitrification, a primary process in reducing nitrate in ground water (Crandall, 1999).
Denitrification occurs in the absence of dissolved oxygen and in the presence of chemically reduced
compounds such as organic carbon or iron sulfide minerals such as pyrite (FeS2). This process is usually
mediated by bacteria, which derive energy from the reaction.
Riparian buffers and wetlands decrease nitrate concentrations and therefore are considered natural
sink areas for N(V. It is important to consider both groundwater hydrology as well as biological processes,
such as plant uptake, nitrogen fixation, and denitrification, in understanding reductions of nitrogen in
riparian buffers. In these areas, denitrification and dilution by discharging ground waters are primary
mechanisms for the reduction of nitrate concentrations (Clausen et al., 2000). Whereas the width of
vegetated riparian strips is the current focus for mitigating N(V contamination, more attention should be
directed to the depth and location of organic-rich riparian sediments, and the groundwater flow path in
influencing the ability of riparian zones to remove nitrate (Devito et al., 2000; Mengis et al., 1999).
SOD controlled diffusion
Figure 5.2. Nitrogen-carbon cycling in soil/sediment derived from animal waste.
Nitrate transport in ground water flowing through aquifer sediments occurs by advection (bulk
motion with seepage flow) and dispersion produced by molecular diffusion and mechanical mixing through
interstitial pore space (Figure 5.3). There is evidence that denitrification may occur at depth in aquifers
when ground waters flow through reducing sediments (reduced iron minerals such as iron sulfide and
organic-rich sediments) under anaerobic conditions (Korom, 1992, Bohlke and Denver, 1995). This process
has the potential of reducing NO3" concentrations in ground water significantly (Hantush and Marino, 2001).
Organic and inorganic phosphorus exist in animal waste. Inorganic phosphate readily adsorbs to soil
particles, limiting its potential for leaching through the soil profile. Inorganic phosphate is the plant-
available form and is a major contributor to eutrophication of water bodies by stimulating algal growth.
Organic phosphorus compounds may be soluble and as such are subject to leaching in the soil (Sweeten,
1991). Most organic forms of phosphorus are readily metabolized to inorganic phosphorus in the soil.
Phosphorus adsorption-desorption reactions in the soil govern release of available P (Siddique et al., 2000).
Phosphorus binds to clays, organic matter, and Fe and Al oxides, which comprise the most easily eroded soil
components (Sims et al., 2000). As such, erosion of soil may generate a P-enriched sediment that may have
effects on deposit!onal areas of water bodies. With continual applications of animal waste containing P, the
soil may become saturated with P and the potential for both erosion and leaching losses increases. Sandy
soils are especially vulnerable to over-fertilization with mineral or organic fertilizers (Sims et al., 1998).
Sandy soils lack the fine- grained materials that adsorb P and hold it in the soil. Macropore flow of water
may also be a mechanism for the transport of P into groundwater and tile drains (Oygarden et al., 1997).
': Interstitial (pore-water)
Figure 5.3. Diagrammatic illustration of preferential flow through macropores and interstitial (pore-water) flow in the soil
Dissolved inorganic P may be higher in concentration than eutrophication thresholds in surface waters
(Ryden et al., 1973, Sims et al., 1998). Managing phosphorus to limit its entry into water bodies is a key
need in controlling pollution from CAFOs.
The fate and transport of microbes in soil and groundwater are controlled by physicochemical
characteristics of the microbe and the soil/aquifer media (Robertson and Edberg, 1977). Key characteristics
of the microbe include size, inactivation (die-off) rate, and surface electrostatic properties, shape, and
specific gravity. Key properties of the soil/aquifer system include soil texture, grain size, porosity,
paniculate organic carbon content, temperature, pH, and other chemical characteristics of water and mineral
composition. Primary mechanisms for the transport and fate of pathogens include advection, retardation,
and mortality. Percolating water provides the advective mechanism for downward movement of microbes
through soil profiles. In saturated flow, water by-passes the filtering effect of the soil matrix and transports
microorganisms long distances in the soil macropores (Mawdsley et al., 1995). Retardation occurs
primarily by natural filtering (entrapment) and adsorption, mainly of hydrophobic nature (Carne et al.,
1980). Retardation effects provide time for inactivation to eliminate the organisms. Entrapment of
microbes by the soil may lead to mortality that is influenced by environmental factors, such as dryness, pH,
predator soil microorganisms, lack of percolation water, and organic matter content (Rosen, 2000). Viruses
are generally more resistant to inactivation and more mobile than bacteria in ground water. Typical half-
lives for microbes in ground water range from a few hours to a few weeks (Robertson and Edberg, 1977).
Greater microbial movement occurs in coarser soils with larger pore sizes. Smaller pore size affects
filtration of bacteria and protozoa more than smaller viruses. Macropores transport microbes to greater
depths in undisturbed soils due to water flow bypassing the main filtering effect of the soil as it flows
through the macropores (Thomas and Phillips, 1979, Mawdsley et al., 1995, McCoy and Hagedorn, 1979).
Irrigation soon after manure application may move fecal coliforms into tile-drains fairly rapidly (Geohring
et al., 1999). Adsorption of microbes occurs primarily onto charged surfaces of clay and organic matter.
Fine-grained soil and aquifer materials have larger surface areas available for adsorption. Due to
hydrophobic partitioning of microbes to organic matter, an aquifer that has relatively high organic carbon
content will tend to retard the migration of microbes more than an aquifer with little or no organic carbon.
The greatest potential movement of pathogens to ground water occurs through sandy soil compared to clay
soil. Microbes move faster in fractured rocks than in granular aquifers, primarily for two reasons. First, the
former conduct flow much more rapidly, thus providing greater advection of microbes than the latter.
Secondly, fractured rocks generally have much less mineral surface area than granular aquifers, thus
exhibiting less adsorptive retardation of microbes.
Retardation of microbes in soils depends on several factors, such as size, shape, surface electrostatic
properties, and specific gravity. Hydrophobic adsorption on to soil organic matter is a much more important
retardation mechanism than soil filtration for most microbes in ground water. Increasing organic carbon
content decreases virus mobility and effectively immobilizes virus migration in aquifers. Because of the
size and surface electric properties, viruses are much more mobile in ground water than Cryptosporidium
and Giardia. Larger microbes, such as bacteria and protozoa, are more susceptible to filtering in soil than
viruses. Hydrophobicity and cell size affect microbial association with soil particles and hence their survival
and transport in soil.
Spatial variation of soil pH and temperature influence the transport and survival of microorganisms
in soils. Adsorption and movement of viruses and bacteria appear to be strongly correlated with increase in
soil pH. Soil temperature affects adsorption and survival of microorganisms through soil. In general, low
temperature favors survival of microbes (Hurst et al., 1980).
Plant roots tend to increase the translocation of bacteria through soil (Kemp et al., 1992, Mawdsley
et al., 1995). Infiltrating water may accelerate movement through root channels. There is evidence that
earthworms enhance transport of bacteria in soils following slurry application (Opperman et al., 1987).
5.3.3 Risk Management
Risk management implies weighing the risks to human health and the environment, against costs
associated with potential alternative management strategies (Rosen, 2000). Design of animal waste and
wastewater storage facilities, and management of manure-based agriculture require the comparison of
associated costs with the risk of groundwater pollution. Measures for groundwater protection may focus on:
1) minimizing seepage of manure and wastewater to ground water; and 2) implementing nutrient best
management by adopting specific farming practices.
5.3.4 Storage Facilities
Manure and wastewater may be stored in earthen impoundments (e.g., lagoons) or underground
storage tanks. The use of lined lagoons or closed storage tanks depends on site-specific conditions (soil,
hydrogeology, climate, and geography), available material, and economics. Leaching of pathogens or
soluble pollutants such as nitrate from earthen impoundments and leaky underground storage tanks
constitutes a major concern when the potential of groundwater pollution is a primary component of the risk-
management criteria. In general CAFOs should be located away from areas with high leaching potential,
such as highly permeable underlying bedrock and soil (EPA, 2001). For example, lagoons should be
located on soils with low to moderate permeability or on soils that may form a seal through sedimentation
and biological action. Most CAFO facilities are either paved or highly compacted, and therefore relatively
impervious. Seepage from storage facilities may be minimized by soil compaction, self-sealing, liners, and
soil amendment (EPA, 2001). The associated cost varies across the different measures, with concrete and
synthetic liners being the most expensive. A risk-based management approach would require comparing
associated costs with the possibility of failure of alternative measures designed to prevent the potential for
groundwater pollution at an acceptable level of risk.
Self-sealing with manure solids or by fine organic matter and bacterial cells reduces infiltration and
therefore minimizes the leaching potential after a finite period of facility operation (say, a few months).
Although this is the least expensive alternative, early in the life of a facility significant leaching may occur
leading to increased potential for groundwater contamination by pollutants such as nitrate and pathogens.
Relying on self-sealing alone may not be an effective means for reducing leaching potential (Frarey et al.,
1994; U.S.EPA, 1998). Sealing is generally effective for cattle manure and in fine-textured soils (high clay
content). Liners made of concrete, synthetic material, or compacted clay may be needed under some site
conditions (EPA, 2001): 1) a shallow water table; 2) an underlying aquifer used for a domestic water supply
or of ecological significance; and 3) highly permeable underlying soil or bedrock (e.g., coarse sand,
fractured limestone) (Figure 5.4-5.5). Clay-lined lagoons have the potential to leak and impact groundwater
quality (EPA, 1998; Ritter and Chirnside, 1990), since they are susceptible to burrowing worms and
cracking as they age. Appropriately sealed below ground storage tanks are effective means for preventing
seepage of manure to ground water in sites with porous soils and fractured bedrock.
From a watershed prospective, any practice that reduces infiltration or seepage will reduce the
capacity of the soil profile to transmit pathogens and soluble pollutants, specifically nitrate, to ground water.
The optimal choice will ultimately depend on incurred costs and acceptable risk level of potential
groundwater and surface-water pollution.
5.3.5 Farming Practices
Manure is a beneficial soil amendment and contains nutrients valuable for plants; when managed
appropriately this may reduce costs associated with the use of commercial fertilizers. However, stockpiling
and land application of manure in excess of crop requirements carry environmental risks, such as surface
water and groundwater loading of nutrients (Schepers and Francis, 1998). Composted manure improves soil
properties while providing plant nutrients and may save energy by replacing commercial fertilizers; e.g., 3
billion Btu/acre (Deluca and Deluca, 1997). Compost has an advantage over raw manure as it destroys plant
and human pathogens and insect larvae.
Ideal management of manure requires: 1) application of manure at agronomic rates; and 2) site
management (e.g., tillage, crop residue management, grazing management), which minimize nutrient losses
from topsoil and surface water and groundwater loading of pathogens by runoff and leaching. Sound
application rates and timing of application reduces losses of nitrogen, especially nitrate, and phosphorus in
subsurface drainage water (Randall et. al., 2000). Manure should be applied at agronomic rates, frequently
Photo courtesy of USDA NRCS.
Figure 5.4. Concrete manure storage tank. Structures of this type will prevent leakage of waste into groundwater.
throughout the growing season, rather than a few concentrated applications. This will prevent rapid
leaching in coarse-textured soils (high in sand) and avoid runoff in fine-textured soils (high in clay).
Although application of manure at agronomic rates reduces nitrogen transport to ground water, it does not
eliminate the risk for groundwater pollution entirely (EPA, 1998). This is because: 1) nitrate is highly
mobile and may move below the root zone before being taken up by plants; 2) uncontrollable recharge
events, such as rain, may cause leaching of excess nitrogen below the root zone; 3) much of the nitrogen
applied is in organic form; however, when mineralized it is released in an inorganic form (ammonium and
nitrate) potentially available for transport to ground water (not as much if in the ammonium form, due to
adsorption to soil particles); and 4) nitrogen transport is affected by manure application method (e.g., drip
irrigation, spray irrigation, knifing, etc.). Potential transport of nitrate to ground water is greater in areas of
high soil permeability and shallow water tables; thus, application in these areas should be managed
appropriately. A great potential exists for nitrogen mineralization when feedlots are abandoned, leading to
leaching of nitrate through the soil profile to ground water (Mielke and Ellis, 1976). Planting corn and
alfalfa in abandoned feedlots may remove nitrogen as it mineralizes.
Photo courtesy of USDA NRCS.
Figure 5.5. A new lagoon with a synthetic geotextile liner to prevent seepage into groundwater.
Groundwaters in areas of sandy soil, limestone formations, or sinkholes are particularly vulnerable
to pathogen transport (EPA, 1998). Pathogens are also prone to movement via macropores. Tillage in the
zone above tiles disrupts macropores and reduces transport of nutrients and pathogens to tile drains and
ground water (Shiptalo and Gibbs, 2000). Shearing of the macropores by tillage appears to limit microbial
transport (Dean and Foran, 1992; and Randall et al., 2000). No-till soils have higher earthworm
populations, thus more earth-formed macropores (Shiptalo and Gibbs, 2000). Application of manure
immediately after irrigation and in the vicinity of tile drains should be avoided to prevent movement of
pathogens (e.g., fecal coliforms) to drainage effluent (Geohring et al., 1999). Factors that need to be
considered for minimizing the loss of microorganisms in runoff and leaching include (USDA, 2000): 1)
climate conditions; 2) waste application techniques and timing; 3) location of applications.
There is a potential for phosphorus to leach into ground water through sandy soils with high
phosphorus content. Land-applied phosphorus is much less mobile than nitrogen because the mineralized
(inorganic phosphate) form is highly adsorbed onto soil particles. High application rates may result in the
accumulation of particulate and soluble forms of P that are potentially available for transport through
earthworm burrows and other preferential paths to tile drains and the water table.
From a watershed prospective, measures to reduce movement of nutrients and pathogens through the
soil matrix and flow-through macropores (preferential flow) would reduce the potential for groundwater
pollution. This would require sound farm practices focused on application rates and timing of manure
application based on local climatic conditions and location. Different levels of management may be
appropriate for different areas of a watershed. Larger areas where freely draining soils, high manure and
fertilizer N applications are made should occur on the upper boundaries of the watershed. Areas most
susceptible to P loss should not be located near the stream channel and should constitute a much smaller
fraction of the watershed (Sharpley et al., 1998).
5.3.6 Natural Filters
The most common practices to reduce runoff, leaching, and drainage from CAFOs include: 1)
terraces; 2) cover crops; 3) filter strips and riparian buffers; and 4) wetlands.
Terraces reduce runoff and soil erosion. Measures to stop erosion may significantly decrease
particulate and dissolved forms of P loss (Withers and Jarvis, 1998). Cover crops use available nutrients in
soil, especially nitrogen, thus preventing or decreasing leaching. However, terraces depending on soil type
may promote infiltration into ground water. Figure 5.6 shows a terrace built between two fields to limit the
erosion of soil on sloping land.
Photo courtesy of USDA NRCS.
Figure 5.6. Terraced fields to limit the erosion of soil on sloping land.
Filter strips and riparian buffers include grass, shrubs, and trees along the riparian interface with
cropland and pasture. They are designed to intercept undesirable contaminants (e.g., sediments, manure,
pathogens, fertilizers, pesticides, etc.) from surface water and subsurface flows (EPA, 2000). Filter
strips/riparian buffers may be effective treatment of overland and shallow subsurface flows for nitrogen and
particulate phosphorus removal. Managing riparian zones with the intent of mitigating NCV contamination
needs to be refocused on characteristics more important than specific buffer width, such as depth of riparian
sediments, groundwater hydrology in that vicinity, and the location of organic-rich sediments (Devito et al.,
2000). Denitrification and dilution processes are primarily responsible for the removal or reduction of
nitrate in groundwaters discharging through riparian sediments (Clausen et al., 2000). Plant uptake may
reduce nitrate concentrations in riparian buffers.
Wetlands occur when the water table intercepts the land surface near streams. Nitrate is primarily
reduced by denitrification and dilution by upwelling ground water in the wetland area. Constructed wetlands
are low maintenance systems that may reduce nitrate from agricultural drainage in artificially drained
watersheds (Kovacic et al., 2000). Anaerobic conditions in the presence of organic matter promotes
denitrification of N(V, which may be further reduced by plant uptake and mixing with nitrate-free
discharging ground waters.
The role of riparian buffer zones and constructed wetlands as nutrient sinks has implications on
management of CAFOs in watersheds. Given acceptable levels of risk, the management of animal waste
and manure-based agriculture at the watershed scale may be significantly impacted by considering the
potential for removal of nutrients naturally, especially nitrate from subsurface drainage in wetlands and
riparian buffer zones.
6 Air Transport and Deposition
Water and air quality issues are related. There has been a lack of CAFO-related research to deal
with both water and air quality issues in a holistic (systems) approach while maintaining high standards of
confined livestock productivity, animal health, and production cost efficiency (Sweeten 2001; Sweeten et
al., 2000). Concentrated animal feeding operations may consist of open lots or confinement buildings,
manure/wastewater storage or treatment systems, land application areas, and facilities to handle animal
mortalities. CAFOs may generate many types of wastes, which include manure (feces and urine), waste
feed, water, bedding dust, and waste water. Air emissions originate from the decomposition of these
different types of wastes from the point of generation through the management and treatment of these
wastes on the site. The rate at which the air emissions are generated will vary as a result of several
operational variables (housing type, animal species, and waste management system), and weather conditions
(humidity, temperature, wind direction and the time of a wind release). The air emission burden on the
atmosphere is the product of the contaminant concentration and the airflow rate (USEPA 2001).
6.1 Current Air Quality Issues Associated with Agriculture
Six major pollutants have been identified and attributed to air emissions from animal housing areas,
animal waste treatment and storage areas, and application of animal waste to the land. An overview of these
Ammonia is an inorganic nitrogen compound that is easily emitted to the atmosphere from animal
wastes (USEPA 2001). Ammonia is one of the fixed gases of aerobic and anaerobic decomposition of
organic wastes. The major source of ammonia in animal manure is urea from urine or uric acid (in poultry).
During microbial breakdown of fecal material in confinement buildings, on feedlot surfaces, in stockpiles,
and in lagoons or runoff retention ponds, additional ammonia and amines are produced. Ammonia
evolution rates are a function of time, temperature, pH of the manure surface, and level of biological
activity. Ammonia volatilization is probably the most important pathway for on-site loss of nitrogen in
animal manure to air and water resources. When ammonia is present as part of an aqueous solution, it reacts
with acid to rapidly form the ammonium ion, with little release of ammonia to the atmosphere. Most animal
manures, feedlot surfaces and lagoons would typically be a non-acidic environment with a pH greater than
7.0, where a rapid loss of ammonia to the atmosphere will occur. Total nitrogen losses as ammonia may
exceed 50% (Sweeten et al., 2000; USEPA 2001).
Anaerobic lagoon and waste storage ponds are main components of the waste management systems
at many CAFO sites. These systems depend on microorganisms to mineralize organic nitrogen to
ammonium and ammonia. The ammonia will continually volatilize from the surface of the lagoon and
pond. As much as 70%-80% of the nitrogen in a lagoon changes from liquid to gas, which will escape into
the atmosphere in a process known as ammonia volatilization. Depending on the amount of carbon-rich
bedding used, the more carbon, the lower the ammonia emissions. Bedding is used when the manure is not
liquefied, and the bedding with absorbed manure and urine is stored in a solid form. The bedding creates a
porous mixture wherein free air space provides conditions suitable for aerobic microbes to flourish. The
decomposition of solid manure by aerobic bacteria begins a heating process known as composting. This
decomposition process produces heat, water vapor, carbon dioxide, and ammonia. Only ammonia is
odorous, and its emissions are low if the farmers use enough carbon-rich bedding to keep wet spots in the
beds covered and maintain a high carbon/nitrogen ratio in the manure-bedding mixture. The gaseous
ammonia returns to earth, precipitated from the atmosphere by rain or trapped by trees, grass, or water
bodies, in a process known as atmospheric deposition. For example, a typical five-acre hog waste lagoon
releases 15-30 tons of ammonia into the air annually. Approximately half of the ammonia rises as a gas and
generally falls to forests, fields, or open water within 50 miles, either in rain or fog. The rest is transformed
into dry particles that travel up to 250 miles. Ammonia is the most potent form of nitrogen that triggers
algae blooms and causes fish kills in coastal waters. The North Carolina Division of Water Quality
estimates that hog factories constitute the largest source of airborne ammonia in North Carolina, more than
cattle, chickens, and turkeys combined. In 1995, Hans Paerl, a marine ecologist from the University of
North Carolina, reported that airborne ammonia had risen 25% each year since 1991 in Morehead City, 90
miles downwind of the hog belt (Halverson, 2000).
At concentrations found in the livestock facilities (< 100 ppm), the primary impact of aerial
ammonia is as an irritant of the eye and respiratory membranes. The impact of aerial ammonia as a chronic
stressor may affect the course of infectious disease and directly influence the growth of young animals
(Sweeten et al., 2000; Merchant et al., 2002). Ammonia is recognized as a human toxin. Because ammonia
is water-soluble, it is rapidly absorbed in the human upper airways, which results in damaging the upper
airway epithelium. Moderate concentrations of ammonia (50-150 ppm) may lead to severe cough and
mucous production. For example, exposure to 100 ppm for 30-second periods leads to nasal irritation, and
nasal airway resistance increases. Lower concentrations (7 ppm) of ammonia adsorbed to respirable
particles may reach the alveoli (Merchant et al., 2002). Higher concentrations of ammonia (> 150 ppm)
may cause scarring of the upper and lower airways. A consequence of these inflammatory responses is
reactive airway dysfunction syndrome and associated persistent airway hyper-responsiveness. At much
higher ammonia concentrations, the ammonia may pass the upper airways to cause lower lung inflammation
and pulmonary edema. Chemical burns to the skin and eyes may also occur. Massive exposure (in the range
of 500 ppm) to ammonia may be fatal.
6.1.2 Nitrous Oxide
Nitrous oxide is one of the most potent agricultural greenhouse gases that contribute to global
climate change. Nitrous oxide is produced in the nitrogen cycle during nitrification and denitrification of
the organic nitrogen in livestock manure and urine. The emission of nitrous oxide is a function of the
nitrogen content of the manure, the length of time the manure is stored, and the specific type of manure
management system used. Nitrous oxide is released from natural processes in the soil, from nitrogen
fertilizer, fossil fuel combustion, animal and human wastes, water bodies, biomass burning, and land
clearing. The amount of nitrous oxide emitted tends to be small from manure because pH-dependent
environmental conditions are often not suitable for nitrification to occur. Nitrous oxide has over 200 times
the warming effect of carbon dioxide and lasts 150 years in the atmosphere. It is the least prevalent of the
agricultural gases that contribute to the greenhouse effect, contributing only about 3% of the global warming
burden (USEPA 2001;Agriculture and Agri-Food Canada 1998; Halverson 2000).
Methane is colorless, odorless, lighter than air, and is another one of the highly potent greenhouse
gases that contribute to global climate change. Methane has a long residence time in the atmosphere (5-10
years). It is produced during the normal digestive processes of animals and the decomposition of animal
manure. When the organic material from livestock manure is placed under anaerobic conditions, large
populations of methanogenic bacteria are enriched, producting large quantities of methane. The main
factors that influence methane emission from livestock manure are the methane-producing potential of the
waste and the proportion of the manure microbial population able to produce methane. These main factors
will depend on how the manure is stored, treated as a liquid, handled as a solid, and the length of time
before manure deposition on pastures and rangelands. When livestock manure decomposes aerobically,
little or no methane is produced (Merchant et al., 2002; Agriculture and Agri-Food Canada 1998; USEPA
6.1.4 Carbon dioxide
Carbon dioxide is a naturally occurring, voluminous greenhouse gas and is emitted into and removed
from the atmosphere on a continuous basis. Carbon dioxide emissions are produced during microbial
degradation of animal manure under aerobic and anaerobic conditions. When animal wastes are stored as
liquid waste, an increase occurs in the amount of carbon dioxide produced and emitted compared to dry
storage. Carbon dioxide emissions may frequently occur from the combustion of biogas from anaerobic
digesters used to recover energy (USEPA 2001; Halverson 2000).
6.1.5 Hydrogen sulfide
Hydrogen sulfide is a potentially lethal gas produced by anaerobic bacterial decomposition of
protein and other sulfur containing organic matter. This colorless gas with the distinctive odor of rotten
eggs is heavier than air and may accumulate in manure pits, holding tanks, and other low areas in a livestock
facility. The production of hydrogen sulfide is dependent on the outside air temperature, the size of the
housing and waste management areas, the air retention time in the housing areas, and the daily sulfur intake
of the animals. The sources of hydrogen sulfide presenting the greatest hazard in an agricultural setting are
liquid manure holding pits that are commonly located under the slatted floors of livestock facilities.
Although most of the continuously produced hydrogen sulfide is retained within the liquid of the pit, the gas
is rapidly released into the ambient air in small quantities when the waste slurry is agitated to suspend solids
prior to being pumped out. While the concentration of hydrogen sulfide found in closed animal facilities
(<10 ppm) is not harmful, the release of this gas from the manure slurry agitation may produce
concentrations up to > 1000 ppm. Hydrogen sulfide is an irritant gas that produces local inflammation of the
moist membranes of the eye and respiratory tract. Respiratory tract symptoms include irritation of the throat
and a cough. Exposure to concentrations (> 150 ppm) of hydrogen sulfide may impair the sense of smell,
hindering the olfactory detection of high concentrations of the gas. Chronic or acute occupational exposure
to hydrogen sulfide concentrations at elevated levels between 100 - 1000 ppm may cause rapid loss of
consciousness, shock, acute respiratory distress syndrome (ARDS) or pulmonary edema, coma and death.
The primary mode of absorption of hydrogen sulfide is through inhalation. The toxic effects of hydrogen
sulfide are based on its property as a chemical asphyxiate. It binds to the mitochondrial enzyme cytochrome
oxidase, blocking oxidative phosphorylation and ATP production. This leads to anaerobic metabolism and
the development of lactic acidosis (USEPA 2001; Thu 2001; Merchant et al., 2002). Few states, with the
exception being Minnesota, have hydrogen sulfide standards. Other states have different standards
(Sweeten et al., 2000; USEPA 2001; Halverson 2000;Yale Center for Environmental Law and Policy).
6.1.6 Criteria Air Pollutants
Criteria air pollutants include volatile organic compounds (VOCs), and particulate matter (USEPA
2001). Many VOCs are formed when the livestock waste is in a dynamic state, fluctuating between aerobic
and anaerobic conditions. VOCs are formed when the hydrolytic and acetogenic bacteria ferment the
organic matter in the waste. Some of the volatile organic compounds that emanate from CAFO facilities
include acetaldehyde, acetone, acetophenon, acrolein, benzaldehyde, benzene, bis(2-ethylhexyl) phthalate,
2-butanone, carbon disulfide, carbonyl sulfide, chloroform, crotonaldehyde, ethyl acetate, formaldehyde,
formic acid, hexane, isobutyl alcohol, methanol, 2-methoxyethanol, naphthalene, phenol, pyridine,
tetrachloroethylene, toluene, triethylamine, and xylene. Other air pollutants associated with CAFO facilities
include volatile fatty acids (VFAs) and odor compounds. The incomplete anaerobic degradation of
carbohydrate, protein, and lipid components in livestock waste results in the formation of short-chain VFAs
(Varel, 2001). The VFAs produced include butyric, isobutyric, caproic, isocaproic, valeric, isovaleric,
propionic, phenylpropionic, lauric, acetic and phenylacetic acids (Merchant et al., 2002). The odor
compounds emanating from CAFOs include the phenolic compounds, such as phenol, ethyl phenol, and
cresols, and the nitrogen-containing compounds, such as ammonia, amines, pyridines, indole, skatole,
trimethylamine, trimethyl pyrazine, and tetramethyl pyrazine (Merchant et al., 2002).
Paniculate matter is identified as either PM-10 standard (less than 10 |j,m in diameter) and PM-2.5
standard (less than 2.5 |j,m in diameter, referred to as respirable particulate matter). Particulate matter is a
consequence of interactions of animals with their environment. Particulate matter is composed of animal
bedding, fecal matter, litter, feed materials, animal byproducts such as skin cells or feathers, and the
products of microbial action on feces and feed, bacteria, fungi, viruses, metals, and hormones. Components
of feed include plant proteins, starches, and carbohydrates, feed additives such as vitamins, minerals, amino
acids and other supplements, and antibiotics (Merchant et al., 2002).
6.2 Generation of Air Emissions Resulting from Operational Variables
6.2.1 Air Emissions from Land Application Activities
The amount of nitrogen released into the environment from the application of animal waste depends
on the rate and method by which it is applied, the quantity of material applied, and site-specific factors (such
as air temperature, wind speed, and soil pH). The application of animal waste from CAFOs on cropland
generates air emissions. The emissions are the result of volatilization of ammonia immediately after the
material is applied to the land. Additional emissions of nitrous oxide are released from farmlands when
nitrogen is applied to the soil and at the same time the soil is undergoing the process of nitrification and
denitrification. Loss of nitrous oxide through denitrification depends on the oxygen levels of the soil to
which the manure is being applied. Low oxygen levels (as a result of wet, compacted, or warm soil)
increase the amount of nitrate-nitrogen that is released into the air as nitrogen gas or nitrous oxide. For
example, research performed by Sharpe, et. al. (1977), compared losses of ammonia and nitrous oxide from
sprinkler irrigation of swine effluent. The study concluded that the ammonia emissions made the larger
contribution to airborne nitrogen losses (U.S. EPA, 2001). The analysis of air emissions from land
application activities mainly focuses on the volatilization of nitrogen as ammonia, because the emission of
other compounds is expected to be less significant. Figures 6.1 and 6.2 show potential sources for air
emissions of pollutants of concern. High velocity sprinklers may release significant amounts of ammonia
and VOCs into the air as well as generating particulates that may move off site if the wind velocity is high.
Similarly, application of animal waste from tank trucks may release large amounts of odor compounds and
ammonia into the air. Incorporation of the waste into the soil limits losses of odor compounds and ammonia
but increases the cost of application.
In addition to the movement of nitrogen in various forms from land-applied waste, bioaerosols or
particulates of biological origin may move from land-applied waste. Fragments of cell walls, fungal spores,
hyphae, endotoxins, plant cell debris, animal cell debris, and whole cells may all be aerosolized from land-
applied wastes. Little information exists with regard to the importance of organic dust movement in the
Figure 6.1. High velocity sprinkler, a potential source of airborne contaminants.
Photo courtesy of USDA NRCS.
Photo courtesy of USDA NRCS.
Figure 6.2. Tank truck applying manure with the potential for aerosol generation.
CAFOs may affect air quality through emissions of odorous gases (odorants), particulates, and some
of the "greenhouse" gases (carbon dioxide, and methane). The odor may affect the health of, and become a
nuisance to, nearby residents. The odor created from CAFO sources is the composite of > 170 different
gaseous compounds present in livestock manure in trace concentrations above or below a person's olfactory
thresholds. Odor is characterized according to the following characteristics: (a) the strength of the odor (the
concentration or intensity); (b) the frequency of the odor (the number of times the odor is detected during a
period of time); (c) the duration of the odor (the period in which the odor remains detectable); and (d) the
perceived offensiveness, character, or quality of the odor. Some of the general approaches in estimating the
strength or intensity of livestock manure odors are: (a) sensory devices (e.g., scentometer, dynamic
olfactometers, absorption media, etc.) that involve collecting and presenting odor samples (diluted or
undiluted) to trained evaluators under controlled conditions; (b) direct or indirect measurement of
concentrations of distinct odorous gases; and (c) electronic "nose" devices, a series of gas sensors combined
with pattern recognition software to mimic human olfactory responses. The electronic nose device registers
the presence, concentration, or activity of selected odorous gases. Odor frequency and duration are partially
governed by climatic conditions, in addition to atmospheric stability, moisture conditions, and wind-
Anaerobic degradation involves the reduction of complex organic compounds to a variety of odorous
VFAs by acid-forming bacteria. Methane-forming bacteria convert VFAs to odorless methane and carbon
dioxide. If these anaerobic processes are in balance, most odorous compounds are eliminated. However,
under certain conditions in manure storage or overloaded anaerobic treatment lagoons, acid-forming and
methane-forming processes are not in balance, resulting in an accumulation of VFAs. Also, sulfate-
reducing bacteria found in anaerobic environments convert sulfate to hydrogen sulfide and other sulfur-
containing compounds. Anaerobic degradation by sulfate-reducing bacteria and an imbalance of acid- and
methane-forming bacteria are significant sources of odorous compounds (Midwest Plan Service).
Jacob son et al., evaluated odor and hydrogen sulfide concentration in air from 60 different pig, dairy,
beef, and poultry manure storage units on farms. A low correlation was found between hydrogen sulfide
and odor concentration for manure storage based on a species comparison and for production systems
grouped according to manure management system type (basin, lagoon, and pit) (Zahn et al., 1997, 2001).
6.2.3 Particulate Matter
Paniculate matter is solid matter or liquid droplets less than 100 |j,m in diameter from dust, smoke,
fly ash, and condensing fugitive vapors that are carried in the outdoor air. Air quality standards have been
developed to protect public health from the potential effects of particulate matter less than 10 microns (PM-
10), and particulate matter less than 2.5 microns (PM-2.5) in size (Nebraska Dept. Environ. Qual., 2001).
When humans or animals inhale dust, a higher proportion of small particles than large particles will travel
deep into the lung and be deposited. In general, finer particulate fractions contain a higher proportion of
anthropogenic dust and lower levels of wind blown soil and plant pollens. Because lung problems
associated with CAFOs include airway disease, it is important to consider inhalable particulate fraction and
PM-10 (Merchant et al., 2002).
Bioaerosols are a major component of the particulate matter from CAFOs. Bioaerosols are simply
particles of biological origin that are suspended in the air. Bioaerosols include bacteria, fungi, fungal and
bacterial spores, viruses, mammalian cellular fragments, pollens, and aeroallergens, toxins, and particulate
waste products. Bacterial products or components exist as bioaerosols and include endotoxins, exotoxins,
peptidoglycans, lipoteichoic acids, and bacterial DNA bearing CpG motifs. Fungal products or components
include conidia and microconidia, hyphal fragments, mycotoxins and glucans. Various concentrated animal
feeding operations are sources of bioaerosols because of the feed material used, the fecal material produced,
and the type of bedding material used (Merchant et al., 2002).
Bioaerosols are a respiratory threat to workers performing waste management activities at
concentrated animal feeding operations. Inhalation of pathogenic microorganisms may result in an acute
disease, with full-blown infections. For example, acute endotoxin inhalation exposure may result in
influenza-type symptoms. Chronic endotoxin exposure has been associated with decreased respirometric
values (e.g., hypersensitivity pneumonitis) in workers associated with concentrated animal feeding
operations. Several studies describe "Organic Dust Toxic Syndrome," which is a health effect associated
with particulate exposure (such as asthma).
Some CAFOs have installed engineering controls, (such as ventilation systems) to lower worker
exposure to bioaerosols. These ventilation systems will discharge a relatively high concentration of
bioaerosols to the environment, unless air treatment unit processes are also installed. The ventilated
aerosols that are not treated may cause an air plume to travel beyond property lines. Several factors will
determine the downwind concentration of a CAFO generated bioaerosol, some of which include: (1) the
distance to the property line; (2) the wind velocity and direction; (3) the biological half-life; (4) the
humidity; and (5) the amount of ultra-violet light present. There were not any studies in the literature that
evaluated public health exposure beyond a reasonable distance from a CAFO system.
Since the early 1970's, very little consideration has been given to air quality protection with respect
to agriculture. This has resulted in very little data existing to determine agriculture's impact and
contribution to air quality. Significant issues related to agriculture and air quality were presented and
informational gaps were assessed to determine the type and amount of resources needed to address issues
related to air quality and agriculture.
Animal and production agriculture may produce emissions of odorous gases such as ammonia,
hydrogen sulfide, volatile organic compounds/acids, and particulate matter. Current knowledge does not
fully describe or reflect potential air emissions produced from these pollutants.
7 RISK MANAGEMENT OPTIONS FOR CAFO WASTE
Now that the risks associated with the large amounts of animal manure present at CAFOs have been
described, this document will now discuss what may be done to mitigate CAFO manure pollution. This
section will be divided by strategies that are well known, those requiring some additional research, and
those strategies that are new and innovative and require significant additional research to fully implement.
Within each section we will describe how the strategies discussed will mitigate each of the stressors
identified in this document: nutrients, pathogens, EDCs and antibiotics.
Two well known risk management strategies, discussed in detail below, are land application and
composting. Land application is the main means by which animal manure from CAFOs is disposed. This
often results in excessive application that results in release of manure stressors into the environment. This
makes land application part of the problem. It may also be part of the solution if done properly.
7.1 Land Application
This section summarizes the benefits and risks associated with land application of CAFO waste.
Application of animal waste to land presents a complex set of topics for consideration. Animal manure has
been applied to soil primarily as a disposal operation since the Roman Empire. Similarly, use of animal
manure to enhance soil fertility has been known for about as long, but the underlying reasons were only
illuminated within the last 150 years. Manure as a fertility agent has several benefits for agricultural
production. The advantages come from the value of animal manure as a fertilizer and soil conditioner
(Kellogg et al., 2000; USDA/NRCS 1996,1998; Weidner et al., 1969). The nitrogen and phosphorus
content of manure has a real value, when substituted for inorganic chemical fertilizer (Bitzer and Sims,
1988;Edwards and Daniel, 1992). The soil conditioning aspect is important. As soil organic matter
increases, soil workability improves leading to lower power requirement for equipment. Water holding and
infiltration improve leading to greater drought resistance. Nitrogen, phosphorus, and potassium are recycled
into the soil with applied manure, thus maintaining fertility. Major portions of N and P in manure are in
organically bound components, which function as slow release nutrient sources. The organic matter
component of manure maintains or enhances the soil organic matter fraction. The benefits of manure
application to soil are well recognized. For most purposes the smaller farm operations may gain the benefits
with relatively minor problems.
The liability comes from the need to have adequate land for disposal/treatment, the cost of
application including capital costs, labor and transportation costs and the potential environmental liability,
should a nearby water body be contaminated by wastes. The task of balancing the advantages and
disadvantages lies in successfully measuring the nutrient content of manure and calculating application rates
(Iowa State Univ. 1995; Maguire et al., 2000; USDA 1979; USDA/NRCS 1996,1998; Weidner et al., 1969).
Allowances must be made for the available N from manure, losses to atmosphere as NH3, and potential
variation in application. Managing application by N content usually results in over-application of P.
Managing by P content under supplies nitrogen leading to a need to add inorganic N. Since there are
differences in application equipment for manure or inorganic fertilizer, that portion of costs increases.
Every segment of animal agriculture production has examples of waste load exceeding the
absorption capacity of the local environment. As discussed in the beginning of this document, the problem
derives from concentration of production facilities into relatively small land areas, with little space available
for waste disposal. Some facilities market the waste as fertilizer material, but the transport distance
becomes the limiting economic factor (Bosch and Napit 1992). The key question for consideration in this
risk management evaluation is how to properly use land application to reduce the risk to water quality from
CAFO manure while still realizing its many tangible benefits. Answering this question requires an
examination of how manure is currently used and how it may be used more efficiently.
Numerous documents exist providing guidance to the farm operators on every aspect of application
of manure to soil. There are documents produced by the USD A, States, and universities that provide
examples of how to calculate the fertilizer value of different wastes. The publications provide models of
how to substitute manure for inorganic fertilizer to meet yield goals. The key factor is that every facility
presents a unique situation with regard to soil type, waste type, soil conditions, erosion potential, and
climate. There are no universal solutions for using CAFO wastes as a fertilizer source. Some general
principles do apply however. Application rates should be based on the more restrictive crop phosphorus
requirements. Waste application should be timed to provide maximum benefit for crops. Manure should
not be spread on land in winter where the ground is frozen. Wherever possible, incorporation should be
done within 24 hours of application. Soil management to minimize erosion will help mitigate any runoff
problems associated with manure. This section is intended to provide an overview of the practices used in
land application, some of the problems attendant with land application, and some management practices to
minimize problems. The literature citations provided represent a small fraction of available material
concerning the subject.
7.2 Practices Used in Land Application
7.2.1 Application Systems
Transport of manure from the site of production or storage to the fields where it is applied may take
many forms. Some are simple load and spread systems. Some are more complex with mixing, shredding,
pumping and distribution machinery involved. The type of system used varies with the characteristics of the
waste being handled. Different animal production facilities have elected different waste handling modes
that are most commonly based in ease of operation and cost. Liquid manure application may take several
forms (Doughherty et al., 1998). Tractor drawn or truck mounted tank systems may either broadcast or
directly inject liquids (Figure 7.1). Tractor pulled broadcast or injection applicators can be supplied by drag
hoses or temporary holding tanks. This option reduces potential soil compaction.
Irrigation application may be flood type, gated channels, or various kinds of sprinkler systems.
Sprinkler systems may be manually moved, fed from a central pumping station; fixed installation; or center
pivot type with central pumping. Use of irrigation type systems may be limited to larger facilities in some
cases simply because irrigation systems need a minimum flow volume to function properly. A major
drawback to spray irrigation systems for the application of liquid manure is the loss of NH4-N to the
atmosphere as NH3. The value of the N is lost and the odor potential is high for sprayer systems. Irrigation
may serve two functions, one to supply nutrients and the other to supply water to meet crop needs. In some
ways, liquid systems may be more limited than others. Installed irrigation equipment is not easily moved;
therefore, the same land is repeatedly treated with manure. Other nearby land potentially suitable for
receiving manure may be passed over.
The major animal production sectors use different waste handling systems. Factors involved in the
elected choices vary from locale to locale. Available data are limited and apply to large production
facilities. Some examples of manure distribution systems are listed in Figure 7.2.
Photo courtesy of USDA NRCS.
Figure 7.1. Tractor drawn liquid manure application after corn harvest.
Means of Manure Disposal
| | Haul Away
Figure 7.2. Means of manure disposal by animal sector.
7.2.2 Potential Problems Associated with Manure Applications
Although the problems associated with nutrients, pathogens, EDCs, and antibiotics in manure are
common to all species of livestock, some additional problems are posed by the way in which the manure is
disposed. This is related to the moisture content of the manure, which is related to the species of livestock
in question. As shown in Figure 7.2, almost all of the manure generated by poultry facilities is sent off-site
for disposal. Environmental pollution resulting from runoff is probably not a big problem at these facilities
as a result of this practice. Nevertheless, myriad problems could result from the off-site transport of poultry
waste because the nutrient and pathogen load of the waste will be out of the direct control of the originating
Over-enrichment with N and P may occur when liquid waste is sprayed on land as is done at swine
CAFOs. Air pollution may result from volatilization of NH3 when downwind transport occurs as a result of
spray irrigation using liquid waste and wastewater. Runoff of oxygen demanding substances, nutrients, and
pathogenic organisms to water bodies may accelerate eutrophication of receiving water and spread
pathogenic microorganisms throughout the watershed. (Baxter-Potter and Gilliland, 1988; Culley and
Phillips, 1982; Doran and Linn, 1979; Doran et al., 1981; Edwards and Daniel, 1992; Gagliardi and Kerns,
2000, Giddens and Barnett, 1980; Gilley and Eghball, 1998; Jawson et al., 1982; Larsen-Royce et al., 1994;
Pell 1997; Smith et al., 1985; Wolf et al., 1988).
Transport of nutrients and microorganisms to groundwater may also occur from both the application
of liquid waste and the spreading of solid manure on land. Another avenue for nutrient losses exists in the
leaching of soluble nutrients either to groundwater or drainage tile (Entry and Farmer, 2001; Evans et al.,
1984; Gangbazo et al., 1995; Simpson 1990). N applied in manure as NFLt+ will exchange on to soil cation
exchange sites. This form of N does not readily move, but may be nitrified to NO2" and NO3" (Eghball
2000) that are freely mobile in soil water. Subsequently, denitrification may reduce the N(V NO2 to N2O or
N2 (Rochette et al., 2000; Stevens et al., 2001)
Even the subsurface injection of solid manure may contaminate water sources as the result of
channel flow through the vadose zone. The channels may take the form of worm burrows, root channels, or
animal burrows. P usually rapidly converts to insoluble forms, but with high application rates and rainfall,
P will move as soluble P. Water-soluble organic N and P may also move into groundwater or drainage tile.
Movement of NCV into groundwater may increase N(V levels above the federal standards of 10 mg/L. Too
much NO3" in water presents a risk to very young children by causing methemoglobinemia (already been
said). Loss of N and P to drainage tile primarily represents loss of the fertilizer value of the applied manure.
It also increases the potential for eutrophication of receiving waters.
The bacterial load of animal waste either applied to the soil surface or injected below ground may
enter the channels existing in the soil and migrate into drain tile. If water flow is relatively large, the water
may transport organisms including pathogenic organisms to receiving streams, lakes, or ponds. This
pathway is easily overlooked as it is assumed that water entering drain tile has been filtered through the
overlying soil. Studies of the movement of bacteria through the soil profile are recent. Entry and Farmer,
2001 examined coliform and nutrient movement in a sand aquifer below fields irrigated with river water.
Smith et al., (1985) also showed that E. coli could move through soil most easily in undisturbed soil
columns. Tilled soil was more effective in retarding the movement of the organisms. Gagliardi and Kerns,
(2000) reported that E. coli O157:H7 could move through agricultural soils under different management
practices. Patni et al., (1984) studied the bacterial quality of water in tile drains under manured and
fertilized cropland. Their results showed that bacteria could move easily through the soil profile. Shipitalo
and Gibbs, (2000) showed that injected manure could move to tile drains within minutes of application
through worm burrows. The width of the transmission zone was about one meter at the soil surface.
Because movement of microorganisms through soil profiles has been observed, it is also likely that
EDCs and antibiotics may move with the water flowing through the same channels that allow passage of the
7.2.3 Soil Management Practices to Reduce Problems
Control of potential pollution from land-applied manure requires attention to good soil management
practices (Cook et al., 1996; Dillaha et al., 1986; Young et al., 1980). Soil management to reduce erosion
losses will reduce potential manure runoff losses of oxygen demanding compounds, N, and P. The most
important factors contributing to or limiting erosion include: degree of slope, susceptibility of soil to
detachment, crop cover, rainfall, and presence of erosion control practices (Cook et al., 1996; Dillaha et al.,
1986; Liu et al., 2000).
7.2.4 Runoff Control from Land Application Fields
Runoff from the immediate CAFO operation is best controlled at the source as described above.
However, runoff control in a land application of animal waste is not as easily managed. The large areal
coverage typical in land application makes management of the waste more difficult. In most applications,
the primary stressor of concern will be the nutrients. Nitrogen as found in animal waste is soluble and will
be transported via the water (Eghball 2000). Phosphorus,, however, is particle-bound and will be
transported through erosion and sediment transport. Effective controls for phosphorus will require measures
to prevent the detachment, transport, and deposition of soil particles to a receiving water. Typical erosion
control strategies may be used to minimize the SSAS and associated stressors delivered to a water body.
In a land application of waste, the most effective management for SSAS is to retain the soil and
solids applied to the field. There are three primary points to reduce the SSAS from land application: 1)
reduce soil detachment, 2) reduce transport within the field, and 3) trap sediment after the field.
22.214.171.124 Reducing Soil Detachment
To effectively reduce the soil particle detachment, the energy from a falling rain droplet must be
adequately dissipated. Crop cover and crop residue may dissipate energy to varying degrees depending on
the extent and type of coverage (Woo et al., 1997). Accepted conservation practices such as conservation
tillage, cover crops, contour farming, buffer strips, riparian buffer, and effective pasture management may
significantly reduce the soil detachment due to direct rainfall.
Conservation tillage reduces vulnerable soil exposure by maintaining a cover crop and/or crop
residue on the soil surface. Examples of conservation tillage include preparation of seedbed bands only for
rowcrops, chisel plowing or disking to incorporate plant residues vertically into the soil surface rather than
turning under as with a traditional plow. Approximately 45% of crop production in the US occurs with
conservation tillage. Use of reduced tillage is not conducive to incorporation of applied manure. Similarly,
tillage of pastureland or hay production field would not be done. Chisel plow type injection could be used
on these lands to a limited extent. Leaving crop residues on the soil and planting cover crops will reduce
raindrop impact on the soil, thus reducing the detachment of soil particles that could erode.
On sloping land, contour strip fields may be used to control water flow (Liu et al., 2000). Alternate
strips of different crops are planted perpendicular to the slope to reduce water velocity and retain sediments.
Crop rotation may reduce runoff by including a hay type crop between row crop years. The potential soil
erosion from hay is much less than row crops. Provision of buffer zones, terraces, filter strips, and
windbreaks may all reduce soil erosion by slowing the speed of water and wind across the soil surface.
These measures may also collect particulates in motion, preventing them from reaching larger streams.
Proper pasture management may reduce pollutant movement. The best time to apply manure to hay
acreage is subsequent to removal of the last crop. Then there would be a substantial time for the manure to
be absorbed with little risk of bacterial contamination of harvestable crops. Similarly, manure may be
applied to wheat and oat fields after harvest of the grain and straw. The manure could be absorbed prior to
seeding of the next crop or as the soil is prepared for the next crop.
Atmospheric losses of N may be curtailed by incorporating manure either by direct injection or by
tilling within 24 hours after application. For some crops, the incorporation of manure may be combined
with preparation for seeding. One factor in reducing NHa volatilization from soil is that most agricultural
soils have pHs in the range of 6 to 7.5. Ammonia will tend to remain in soil at that pH.
126.96.36.199 Reducing SSAS Transport within a Field
To effectively reduce the transport of SSAS within a field, techniques to minimize runoff, increase
infiltration, and trap sediments are used. Similar conservation techniques described for reducing soil
detachment may also reduce the within-field transport. The use of cover crops and crop residue will
effectively reduce the runoff velocity and trap sediments. The type and extent of cover crop or crop residue
will control its effectiveness. Contour farming, strip cropping, and conservation tillage may all effectively
reduce within-field transport. Diversion of runoff from up-slope areas may also reduce the runoff on the
Cover crops also immobilize nitrogen and phosphorus effectively converting the elements into
slower release forms. Along streams, other management practices may be implemented to reduce the
potential for eroded material to enter the water. Riparian buffers of trees, grass, and shrubs may reduce
transport of material to the stream. They are discussed in more detail in the next section.
Many agricultural areas of the United States require drainage of the soil by tile to be fully
productive. In those areas, limiting of the amount of applied nutrients would be the best way to control the
movement of nutrients to drainage paths. Areas of the US that have significant karst landforms are also
susceptible to significant losses of N and P in drainage water (Stoddard et al., 1998). Some of the soils are
quite shallow and may rapidly allow movement of water and dissolved nutrients to streams and lakes
188.8.131.52 Trapping Sediment after the Field
The final point of control is trapping sediment after the field. Though this should effectively reduce
the sediment load to a water body, this technique is treating the symptom and not addressing the problem.
Efforts should be made to reduce the generation of SSAS, not simply trap or intercept them. Trapping
strategies include grassed buffer strips, diversions, detention basins/ponds, riparian buffers, terraces, and
wetlands. These solutions generally approach a more engineered solution versus the first two phases of
erosion prevention (preventing soil detachment and within-field transport). Efficiencies vary based on
design and operation of the control structure (Butler and Karunaratne, 1995). In addition, many of the
strategies have multiple functions in the prevention of erosion as shown as in Table 7.1. These strategies are
used alone and in combination to address the erosion problem.
Table 7.1 Functions of soil conservation practices (Adapted from USEPA, 200la).
„ .. _ .. Soil Within Field Sediment
Conservation Practice T-» * i, * T, . n * *•
Detachment Transport Retention
Contour or Cross-slope Tilling
Contour strip cropping/Contour Buffer strips
Depending on topography, waterways on a farm could lead to sediment traps or constructed
wetlands that would intercept much of the sediment and nutrient load that leaves the fields. Periodic
cleaning of these structures would be necessary to retain capacity.
Riparian zones are areas usually associated with the banks of river or stream corridors and are areas
where subsurface flow (groundwater runoff or base flow) reaches either the ground surface or near surface
before contributing to stream flow, causing elevated water tables and high soil moisture condition that
typically support a variety of vegetation. Riparian zones impart a variety of beneficial influences upon
streams such as reducing sediment and nutrient loads, mitigating the severity of flooding, and increasing soil
permeability and soil organic content.
In addition to the physical benefits just mentioned, riparian zones may also exert a chemical
influence on groundwater runoff, most notably conditions that favor nitrate reduction. The ability to support
nitrate reduction is closely tied to the geology and hydrology of a watershed, and the extent of the riparian
If the soils in a riparian zone are saturated, and anaerobic or anoxic conditions exist, nitrate reduction
is possible. In addition to the favorable conditions noted, not only must the flow path of groundwater
intersect or flow through the riparian zone before discharging to the stream, but also the area where
groundwater recharge occurred must be in an area where elevated nitrate levels exist in the soils. In other
words, recharge to the groundwater system may occur over a large portion of a watershed or field, but not
all of this recharged water will follow a flow path through a riparian zone. Some of the water may move
into deep groundwater flow regimes, well below the influence of the riparian zone and into another
groundwater system. Some groundwater may appear as spring flow, also bypassing the riparian zone. Still
other groundwater may follow a flow path that travels below the riparian zone (rather that laterally through
the riparian zone), then vertically upward into the stream minimizing any contact time within the riparian
Seasonal variations also affect the influence of the riparian zone. During wet seasons, the water
table may be elevated and intersect the stream creating the favorable conditions for nitrate reduction.
During drier periods, the water table may drop, and groundwater runoff that previously would have
followed a flow path through the riparian zone will now flow beneath the zone without any reducing effects.
Finally, even if the flow path that groundwater runoff follows is lateral through the riparian zone, only
runoff that originates in an area that has elevated nitrate will experience possible nitrate reduction. This
becomes important when areas are chosen for the application of animal waste. If the goal is to incorporate
the benefits of a riparian zone into the management of animal waste, the waste must be applied in areas
where the runoff generated, both surface and subsurface runoff depending on the benefit desired, will flow
through the riparian zone.
The two primary nutrients in animal waste behave almost opposite to runoff or precipitation.
Phosphorus (P) is primarily transported as particulate P in runoff, although there is an important component
of soluble P, whereas nitrate is highly soluble and is more readily leached into the groundwater. As noted
previously, this may be a factor in deciding where to place animal waste within a field or watershed.
Precipitation events that are insufficient to produce runoff that would carry P to a receiving water body are
typically insufficient to mobilize sediments. Finally, even if the flow path that groundwater runoff follows
is lateral through the riparian zone, only runoff that originates in an area that has elevated nitrate will
experience possible nitrate reduction.
7.3 Composting of CAFO wastes
Composting of CAFO and AFO wastes benefits the environment because nutrients contained in
manure, livestock carcasses, and other materials are converted to stable forms in the compost. Therefore,
these nutrients are less likely to leach into groundwater or to be carried off with surface runoff. In addition,
the total mass of material is reduced in the composting process. Compost may be easily stored until
conditions are favorable for land application and therefore possibly minimizing the impact to
environmentally sensitive areas. Another advantage of composting is that due to high self- heating (55-
65°C), the process is generally self-pasteurizing for most pathogens, provided that the minimum time and
temperature conditions have been met. The main concerns of composting these types of wastes are pathogen
control, nitrogen volatilization and leaching, excess available phosphorus, and economic viability of
composting depending on type of system required.
7.3.1 What is Composting?
Composting is a useful tool in waste management because it may rapidly transform putrescible
material to a stabilized product that may be stored, transported, and used as a soil conditioner/fertilizer (May
nard 1993). In composting, a solid-phase organic material such as manure mixed with a bulking agent (corn
cobs, corn stover, straw, wood chips) serves several functions. The solid organic phase is a physical support
for microorganisms, maintains pore space for gas exchange, is a source of organic and inorganic nutrients,
contains diverse indigenous microbes, and provides thermal insulation. Water may be added to maintain the
proper moisture content of the compost. The major form of microbial metabolism is aerobic respiration.
The heat generated during the exothermic reactions of metabolism becomes trapped within the matrix
causing self-heating, which is characteristic of the composting process. The critical elements of successful
composting are a proper carbon to nitrogen ratio (15-40 to 1), adequate oxygen supply, temperature control,
maintenance of moisture, and provision of an adequate time period to reduce pathogens to appropriate
levels. All composting systems may be described by their means of regulating the initial oxygen supply and
maximum temperature (Finstein and Hogan 1993). For a more in-depth review of all the possible
composting configurations based on oxygen supply and maximum temperature, along with a brief
discussion of whether that type of system is currently practiced and, if practiced, how the technology is
faring, see Finstein and Hogan (1993). For a review of the composting process parameters for animal
wastes or other organic wastes, see the following references: Agriculture Waste Management field
handbook by the U.S. Dept. of Agriculture and On-farm composting handbook by NRAES-54 (Dougherty
1999, Rynk 1992.
7.3.2 Composting systems
In order to avoid a long and lengthy list of composting systems in practice and vendor specification
to define composting systems, the basic outlook of man over mechanical intervention required to compost
will be discussed in order to save space. The current practices and system types utilized by poultry,
cattle/dairy, and swine will be discussed later. There are basically two types of composting systems,
interventionary and non-interventionary (Stentiford 1993).
184.108.40.206 Interventionary Systems
Interventionary systems are systems that require mixing as an aeration process, and these systems
may also have some form of supplementary aeration. These systems may take many forms such as
windrows, agitated bays, stirred vessels, and multi towers. The main advantage with interventionary
systems is that mixing of the waste prior to composting is not as critical as it is in non-interventionary
systems. These systems are better suited for the composting of putrescible wastes because they allow the
composter to adjust parameters, such as moisture and amount of bulking agent, while the composting
process is ongoing.
220.127.116.11 Non-interventionary Systems
In non-interventionary systems, the initial conditions of the feed material are critical for successful
operation. Non-interventionary systems consist primarily of aerated static piles and silo systems. The silo
system was not proven to be an effective method of composting due to aeration and moisture control
problems inherent with the system design. The aerated static pile has proven effective with composting
many wastes, but it must be emphasized that this system is not dynamic. The system must be carefully
constructed in order to provide uniform heating and moisture throughout the process since no other
intervention will occur. This means that the risks of composting failure to achieve the desired results of
pathogen destruction and nutrient stabilization are higher with this type of system (Lufkin 1996, Mathur
1990, Sartaj 1997).
7.3.3 Comparison of Interventionary and Non-interventionary Systems
Each type of system has its merits and associated cost. The interventionary systems offer the
operator improved control, shorter processing time, and reduced land use, but with these advantages comes
increased price of setup and operation. The non-interventionary systems offer the operator low setup and
operational costs but requires increased land usage, increase in the time required for stabilization, and little
or no control of the process (Stentiford 1993, Sartaj 1997, Vuorinen 1999-1997). Therefore, the type of
process utilized to compost the CAFO and AFO waste streams must take into consideration the time frame,
costs, distance to population centers, and the systems' ability to meet final regulatory requirements.
7.3.4 Composting in the Beef and Dairy Industries
Since manure from the beef cattle occupying range and pastureland is dispersed by the animals,
composting in the beef cattle industry is limited to manure generated at feedlots (Kashmanian 1996).
Composting is generally performed by the feedlot owners or sub-contractor at the facility. The windrow
method of composting is the most commonly practiced method (Lufkin 1996, Rynk 1992, Mathur 1990).
The manure may be composted alone or by mixing the manure with locally available carbonaceous
feedstocks, such as straw, newspaper, or yard trimmings. The additional carbon sources help in raising the
C/N ratio and reduce the loss of nitrogen as a result of ammonia volatilization (Hong 1997, Larney 1999).
The handling of the material is usually performed by either a front-end loader or a windrow turning
machine. The final compost is either sold commercially for landscape and gardening or sold in bulk for
The sources of manure readily compostable from the dairy industry are the bedding materials used in
barns and partially dried manure from the open lots. Another source of material found in the dairy industry
is manure solids separated from liquid collection systems. Dairy wastes from bedding and open lots may be
composted as is, but the composting process benefits from the addition of high carbon substrates in order to
minimize nitrogen loss due to volatilization (Hong 1983, Hong 1997). As with beef cattle, the method of
composting applied by dairy farmers is windrows. The windrows are either static or forced aeration with
turning methods as described above. The forced aeration systems are generally used by larger facilities that
do not have the land or storage ability to deal with nutrient management issues due to the high manure load
(Joshua 1998, Fernandes 1997). Some composting at dairies is performed by outside organizations and sold
to commercial outlets. The dairy industry has recently adopted some practices that do not favor composting
as a waste management practice. These practices are the use of bedding mats or sand in free stall areas, and
many larger farms are switching over to liquid manure handling systems. The liquid systems increase the
cost associated with dewatering solids and increase the amount of carbonaceous materials needed to
compost. Another disadvantage of these practices is the increased moisture present at the initiation of
composting requires that the compost must be turned more frequently until the moisture level becomes more
favorable (40-50%). If the moisture level remains too high then the composting system has a tendency to
become anaerobic which leads to the production of foul odors (Kashmanian 1996).
18.104.22.168 Composting Swine Waste
Due to the wet nature of swine waste and the current practices of water waste collection the swine
industry is the least suited for composting. A small number of operations raise swine in a deep bedding
method in which the waste is absorbed by straw or sawdust. After the swine are raised, this bedding
material may then be composted by any number of means (Hong 1998, Lau 1993, Peterson 1998,
Tiquial997-98). Most other systems use a liquid method for waste collection, and, therefore, the solids
need to be removed from the waste stream in order to compost. The separation may be performed by
several methods (centrifugation, screening, and presses) but all methods add to the cost and handling of the
waste (Liao 1993, Kashmanian 1996). Due to the wet nature and the high nitrogen content of the swine
manure, a readily available source of high carbon bulking materials would be necessary in order to compost
this material. One area of composting that is gaining attraction in the swine industry is the composting of
mortalities. This is a relatively inexpensive way to deal with mortalities since the cost of rendering and
number of rendering facilities across the country is declining. Only a limited number of states allow this
form of composting and the accepted methods vary slightly from state to state. The pathogens associated
with the swine industry (Salmonella typhimurium, Streptococcus suis, Bordetella bronchiseptica, Listeria
monocytogenes, Actinobacillus suis, and Actinobacilluspleuropneumoniae) have been shown to be
sufficiently killed by the high temperatures of the composting process (Morrow 1995). The composting of
mortalities is limited to normal fatalities and is not an acceptable method for the disposal of a large number
of animals due to a system failure.
22.214.171.124 Composting Poultry Waste
Poultry manure is readily compostable due to the method of raising animals in confined areas and
the dry nature of the material. This manure generally requires the addition of carbonaceous materials due to
its high nitrogen content (Figures 7.3-7.4). Water must also be added to poultry manure and/or litter to
ensure proper initial composting conditions (Flynn 1996, Hansen 1990, Spencer 1997). One of the
advantages of composting to the poultry industry is the relative small land size of poultry operations, and,
therefore, they do not have adequate land for application of raw manure. Composting allows the poultry
producer to stabilize a waste product on a small area while creating a potential value added product.
Commercial outlets for the finished material are one solution that several producers have utilized (Lufkin
1996). Most poultry operations practice composting of mortalities since it is an environmentally acceptable
practice and other forms of disposal are facing increased restriction and increased cost (Kashmanian 1996).
National standards for the practice of poultry mortality composting are published by the U.S. Dept. of
Agriculture's National Resource Conservation Service. Many state and national guidelines are available on
the web for the composting of poultry mortalities.
Figure 7.3. Mixed compost from turkey waste.
Photo courtesy of USDA NRCS.
Photo courtesy of USDA NRCS.
Figure 7.4. Turkey waste compost with wood chips and feathers.
7.3.5 Composting Concerns and Problems
The type of manure handling practice has a large impact on whether a particular farm is going to
compost or not. Composting is generally practiced on farms that handle their manure in a solid or near-solid
consistency. Composting is rare on farms that utilize liquid techniques for manure handling, such as swine
and dairy operations. There are some exceptions because of solids separations techniques, but these add cost
to the final operation and may therefore be impractical in some operations (Liao 1993). In order to address
the high moisture and high nitrogen content of the waste, a locally available source of carbonaceous
materials must also be readily available (Dougherty 1999, Rynk 1992, Hong 1983). The volatilization of
NH3 is a major concern in the composting of manures because it lowers the fertilizer value of the finished
compost and produces environmental air quality issues.
There has been some study of the effect ofC/N ratio on the volatilization of NH? from poultry and
sewage sludge composting operations (Hansen 1990, Hong 1997, Kirchmann 1989, Larney 1999, Lopez-
Real 1996). In order to minimize the loss of NH?, a higher C/N ratio is more favorable. The use of either a
soil or carbon source cover has also been shown to minimize ammonia volatilization (Hansen 1990).
Another factor that seemed to help in the retention of nitrogen during composting is the recycling of
compost back into the initial feed material. This practice, though, is generally only used to inoculate the
composting system, since it reduces the overall mass loss and requires additional handling of the same
material (Larney 1999, Hansen 1990). No information was found on the nitrogen content of potential
leachate from composting materials.
Pathogens associated with these waste streams fall into two categories, primary and secondary
pathogens. The primary pathogens consist of bacteria, viruses, protozoa, and helminths. When the
composting process is run correctly, it is very efficient at destroying primary pathogens, and exposure-
related infectious disease from primary pathogens among compost workers has not been documented.
(Epstein 1993, Bertoldi 1988). To be effective at pathogen removal the composting process must attain a
temperature greater than 55 C for more than three consecutive days (Choi 1999, Rynk 1992, Bertoldi 1988).
Although there are no federal regulations for the composting of manures, the US EPA addresses pathogen
reduction guidelines, which may be applied to manure, for the composting of biosolids in the September
1989 report entitled "Environmental Regulations and Technology: Control of Pathogens in Municipal
Wastewater Sludge," EPA/625/10-89/006, p21, To be considered a PFRP, the composting operation must
meet certain operating conditions. These regulatory conditions are specific to the method of composting
practice. For windrow composting, the sludge must attain a temperature of 55°C (131°F) or greater for at
least 15 days during the composting period. In addition, during the high-temperature period, the windrow
must be turned at least five times. If the static aerated pile or the within-vessel method is used, the sludge
must be maintained at operating temperatures of 55°C (131°F) or greater for 3 days. This temperature
requirement is effective at removing most, if not all pathogens. The removal of Salmonella and other
pathogens during the compost process has been demonstrated for a variety of animal wastes. Lawson
(1999) showed the removal of pathogens during the composting of poultry carcasses and litter. Lung et al.,
2001, demonstrated the removal of Salmonella and E. coll O157:H7 during the composting of cow manure.
This study showed no removal of either pathogen in reactors held at room temperature. Tiquia et al., (1998)
in a study of pig litter composting Salmonella was reduced from 1700 per gram to below detection limit and
a greatly reduced (not specified) population of fecal coliforms and streptococci. The fecal coliforms and
streptococcal numbers were below the amount found in commercially available potting mixes. The only
primary pathogen of concern is the possible regrowth of Salmonella by reinoculation of unfinished compost
(Burge 1987, Russ 1981, Tiquia 1998). Other pathogens are not addressed in recent literature. This has
been shown to be a possible problem from the composting of biosolids/sewage sludge and therefore could
also be a potential problem in the composting of manures (Burge 1987). There has been some study of the
suppression and regrowth of Salmonella in composts at different ages of material by Sidhu, 2001. In this
study, Salmonella was inoculated into sterilized and regular composts of various ages. Salmonella regrowth
was similar in all sterilized composts, with terminal populations of about 100 per gram. The growth of
Salmonella was suppressed in all non-sterilized composts regardless of the age of the material. The
suppression ability of the compost showed a slight decline with time, and, therefore, more study is needed to
look at the effect of long term storage and regrowth of pathogens. Good composting practices that avoid
cross contamination of raw and finished product alleviates this problem. Storage of compost for 30 days
after the active phase of composting has been shown by Gibbs, 1998, to reduce the number ofGiardia cysts
to below detection limits (<10 cysts/gram).
"Secondary pathogens" fungi and other microorganisms produced during the composting process are
of concern. The largest health threat seems to come from a secondary pathogen, the heat tolerant fungus
Aspergillusfiimigatus, and several related fungi, which cause "aspergillosis" (also known as "farmer's lung"
or "brown lung" disease). This fungus, a well-known product of silage, manure compost, and wastewater
sludge compost, grows well on decaying vegetable matter at temperatures above 45°C, and thus survives
most of the composting process. Infections in susceptible individuals (including those on immuno-
suppressant drugs, antibiotics, adrenal corticosteroids, or with pulmonary disease, asthma, and certain other
infections) may be severely debilitating and even fatal. Such infection appears related to high levels of
"infective units" in dusts, perhaps reflecting interaction with other materials as irritants, because the
organism itself is ubiquitous and not regarded as an off-site or product-related problem (Epstein 1993).
7.3.6 Land Application of Compost
The land application of composted manure has been shown to minimize nitrate leaching into the
ground waters (Figure 7.5). The amount of nitrate leached in reported studies was lower from compost-
amended plots when compared to conventional fertilizer or direct manure application (Dalzell 1987, Grey
1999). In a study of groundwater by Maynard, 1993, when compost was applied at rates to supply all
nitrogen requirements, the compost-amended soils had < 10 mg/kg of nitrate as compared to > 14.7 mg/kg
for conventional fertilizer application. In a reclamation study of forest soils by Insam, 1997, using various
composted and non-composted soil amendments, the nitrate levels below the compost plots were only
increased a small amount, whereas the non-compost plots had a highly elevated level of nitrate present in
the ground water (<150 mg/L). A three year agricultural study by Diez (1997), which compared compost-
amended fields to controls and fields with chemical fertilizers under two different irrigation systems, had
mixed results. Under an efficient irrigation system, the compost and control fields had similar low levels of
nitrate in the ground water, but under conventional irrigation practices (field flooding in Spain) the compost
and chemical fertilizer treated plots had similar nitrate levels. Jakobsen, 1996, performed a pot study
looking at the effects of compost-amended soil on mineral availability, soil conditions, and nitrate
availability after compost application and after additional fertilizer application. There was some nitrate
leaching during winter months from the compost-amended soils after chemical fertilizer was applied but the
amount was significantly less than the non-amended control soils. Jakobsen's study also concluded that if
compost is applied at a rate to supply the phosphorus needs of the crop, the soil's pH was raised, the cation
exchange capacity was maintained, and the soil structure was improved even after a crop had been raised.
Another indicator of the stability of nutrients in compost is the agronomic value for estimating availability
of nutrients from compost. Values for the availability of nitrogen range from 7 to 25 percent, whereas
phosphorus is 100 percent, and potassium is 80 percent for the first year (Grey 1999, Tester 1990, Larney
7.4 A Strategy Requiring Some Additional Research- Anaerobic Digestion
7.4.1 Technology Description
Anaerobic digestion may be defined as the biodegradation of organic materials in the absence of
oxygen. This treatment is particularly appropriate for manure with a high organic (BOD) content. The
resulting product is deodorized, has a substantially lower organic load, and has greater nutrient availability
(N and P) for crops. The process converts dissolved and particulate matter into a gas, which is primarily
composed of methane and carbon dioxide, via a series of interrelated microbial metabolisms (Magbanua, et.
Although different types of anaerobic digester designs exist, only covered lagoons, complete-mix
digesters, and plug-flow digesters may be considered commercially available because they are the only ones
that have been implemented successfully at ten or more sites (U.S. EPA, 2001).
126.96.36.199 Covered Lagoons
For agricultural waste, anaerobic lagoons are the most common and simplest anaerobic digestion
treatment systems (Copeland et. al, 1998; McNeil Technologies, 2000). A covered lagoon digester typically
consists of an anaerobic combined storage and treatment lagoon, an anaerobic lagoon cover, an evaporative
Photo courtesy of USDA NRCS.
Figure 7.5. Truck mounted spreader applying compost to a field.
pond for the digester effluent, and a gas treatment and/or energy conversion system. Following treatment,
the digester effluent is often transferred to an evaporative pond or to a storage lagoon prior to land
application (McNeil Technologies, 2000).
The advantages of covered anaerobic lagoons are the reduction of lagoon odor, exclusion of rainfall
from the lagoon, recovery of usable energy, reduction of ammonia volatilization, and reduction of methane
emissions. There are also significant labor savings involved in handling manure as a liquid and being able
to apply lagoon waters to the land through irrigation (U.S. EPA, 2001c). The limitations of covered
anaerobic lagoons include the cost of installing a cover, or the occasional need for cover maintenance such
as rip repair and rainfall pump-off. Spills and leaks to surface and ground water may occur if the lagoon
capacity is exceeded, or if structural damage occurs to berms, seals, or liners (U.S. EPA, 2001c).
188.8.131.52 Complete Mix Digester
A complete-mix digester is a biological treatment unit that anaerobically decomposes organic waste
using controlled temperature, constant volume, and mixing. These digesters may accommodate the widest
variety of wastes and are generally used to treat waste with 3 to 10% total solids and adequate volatile solids
to produce enough methane to maintain digester temperature (Moser, 2000a,b). The digesters are usually
above ground, heated, insulated, round tanks; however, the complete-mix design has also been adapted to
function in a heated, mixed, covered earthen basin. Mixing may be accomplished with gas recirculation,
mechanical propellers, or liquid circulation. Like covered lagoon systems, digester effluent from complete
mix digesters is frequently stored in evaporative ponds. The outflow is recycled onto cropland.
184.108.40.206 Plug-flow Digester
A plug-flow digester is a heated, unmixed, rectangular tank. New waste is pumped into one end of
the digester, thereby displacing an equal portion of older material horizontally through the digester and
pushing the oldest material out through the opposite end (Moser, 2000a,b). The tank is usually built in the
ground and is long and slim and the ratio of the length to the width should be between 3.5:1 and 5:1 (U.S.
EPA, 200Ic). The outflow may go into an outside storage pond to be held until the manure is recycled onto
cropland (Goodrich, 2001).
Overall, some advantages of anaerobic digestion include the opportunity to reduce energy bills,
produce a stabilized manure, recover a salable digested solid by-product, reduce odor and fly breeding, and
produce a protein-rich feed from the digested slurry (U.S. EPA, 2001). However, the costs of installing an
anaerobic digester that collects the biogas may be quite high. Therefore, their economic viability is often
dependent on the price at which the excess energy may be sold to a local electrical utility (Prairie
Agricultural Machinery Institute, 1997).
Anaerobic digesters are, possibly, the most trouble free, low maintenance systems available for the
treatment of animal waste. Farm-based manure facilities are perhaps the most common use of anaerobic
digestion technology (Lusk, 1998). Properly designed anaerobic lagoons are used to produce biogas from
dilute wastes with less than 2 percent total solids, including flushed dairy manure, dairy parlor wash water,
and flushed hog manure. Complete-mix digesters may be used to decompose animal manures with 3 to 10
percent total solids. Plug-flow digesters are used to digest thick wastes (11 to 13 percent solids) from
ruminant animals, including dairy and beef animals (U.S. EPA, 2001).
Anaerobic digestion is one of the few manure treatment options that reduce the environmental
impact of manure and produce a commodity - energy - that can be used or sold continuously. It is more
extensively used outside of the United States where treatment of animal waste has been a concern for a
longer time (Moser, 2000a,b).
U.S. livestock operations currently use four types of anaerobic digester technology: slurry, plug-
flow, complete-mix, and covered lagoons. As of 1998, 28 digester systems are in operation at commercial
swine, dairy, and caged-layer farms in the United States. Table 7.2 provides a numerical status report of
farm-based anaerobic digesters in the United States. The data excludes 65-70 digesters that were installed
on or were planned for beef farms, and digesters that are primarily university research oriented (Lusk,
Table 7.2. Status of Farm-Based Digesters in the United States
Under construction/planning phase
Planned but never built
During the 1990s, 18 systems were installed - more than doubling the number of successful systems
installed during prior years. In 23 of the 31 systems, the captured biogas is used to generate electrical power
and heat (U.S. EPA, 2001).
Because of the differences in the manure produced from different animals, a system to make
methane from dairy cow manure is quite different from a digester for manure from swine. For dairy cows, a
plug-flow digester system works well for collecting and breaking down manure and capturing the gas
produced from this process. A completely mixed digester is better for swine manure (Goodrich, 2001).
Beyond their ability to manufacture biogas, digester designs based on use of thicker manures may
offer the most benefits of the systems evaluated to date. Plug-flow digestion and its slurry cousin are
economically sensitive to co-product use and other offsets from current manure management practices, but
they are less expensive and technically easier to operate and maintain than a comparable complete-mix
digester. Covered lagoon digesters appear to have economic merit for the large number of swine and dairy
operations in the Southeast and West. Complete-mix digesters generally have higher capital costs and
operating and maintenance requirements than slurry-based, plug-flow, and covered lagoon digesters. This
will generally limit complete-mix digester applications to very large farms or centralized facilities, or to
farms having waste streams with total solid concentrations too low for slurry and plug-flow digestion and to
locations where the climate is too cold to economically justify covering an anaerobic lagoon (Lusk, 1998).
7.4.3 Operation and Performance
The successful operation of a properly designed anaerobic digester is dependent upon two variables,
feed rate and temperature. All other operational issues are related to ancillary equipment maintenance. At
face value, the performance data are not encouraging to a farmer considering whether to install an anaerobic
digester as a waste treatment option. Overall, the chance for failure is approximately 50% in the United
States (Lusk, 1998). Among the types of farm-based digesters actually built, the failure rates for complete-
mix and plug-flow systems are staggering: 70% and 63%, respectively. For covered lagoon digesters, the
failure rate is 22% (Lusk, 1998). However, a properly designed, constructed, and operated anaerobic
digester is a low maintenance system that is very forgiving and not likely to create emergency situations that
can be experienced with many alternative waste management systems (Saele). The failures of lagoons and
the resulting waste spills have brought much of the recent critical attention to animal agriculture, and some
have called for phasing out lagoons (Copeland, 1998).
Historically, one of the major problems with anaerobic digestion has been its unreliability. Because
of the complex association of different types of bacteria, anaerobic digesters are prone to problems and have
a higher risk of breakdown than other systems. The process is also more difficult to control (Cord-Ruwisch,
A review of anaerobic digestion project case studies revealed that the most common reasons for
system failures include poor design and installation and poor equipment specification. Poor equipment and
materials selection are also common reasons for failure. Other reasons that explain the failure of some
anaerobic digestion projects include: insufficient gas production due to build-up from straw and foam, an
inability to heat the digester to the desired level, insufficient insulation and agitation, grit deposition, engine
corrosion, inadequate screening and sedimentation process, engine overheating, valve and pump problems,
and maintenance costs (Lusk, 1998).
The improved reliability of newer systems and increased understanding of the biological systems
that operate in an anaerobic digester suggest that the reliability of systems will continue to improve as long
as lessons of past system failures are heeded (Lusk, 1998).
In spite of the chances of failure, survey farmers who have installed and continue to operate
digesters are generally satisfied with their investment decisions. Some chose to install digesters for non-
economic reasons, primarily to control odor or contain excess nutrient runoff. Farmers have found that the
returns provided from electricity and co-product sales from the digester, however limited, are preferred to
the sunk-cost of conventional disposal that provides zero return on investment. Moreover, without the
environmental benefits provided by anaerobic digestion technology, some might have been forced out of
livestock production (Lusk, 1998).
The anaerobic digestion process must be evaluated and implemented at each site. As a result, few
meaningful generalizations may be made. Factors required for successful project implementation include:
an adequate match of digester type to the farm's manure management program, competent design and
installation, which simplify digester operation and maintenance, maximization of co-product use to enhance
economic performance, and overall, an accommodating farm management and its willingness to incorporate
the uncertainties of a new technology (Lusk, 1998).
7.4.4 Fuel Gas Production
Anaerobic digestion is the only waste management strategy available that provides the option to
recover methane for energy production (McNeil Technologies, 2000). According to the USEPA AGSTAR
Industry Directory for On-Farm Biogas Recovery systems, there are currently 89 agricultural methane
recovery sites operating in the United States. A majority of the units are situated in the eastern region of the
country. The digester technologies used to collect biogas from swine facilities include covered anaerobic
lagoons, complete mix digesters, plug flow reactors, induced blanket reactors, and sequencing batch
reactors. Although a sequencing batch reactor has been used for anaerobic digestion at one swine facility in
the United States, this technology is considered to be experimental (McNeil Technologies, 2000).
Daily biogas production at installed farm-based anaerobic digesters in the United States varies from
24,000 to 75,000 cubic feet, or an energy equivalent of 13 to 42 million British thermal units (assuming 55
percent methane content for biogas). Approximately 35 percent of the volatile solids from dairy manure and
60 percent from swine or beef manure may be converted to biogas and removed from the manure liquid
(U.S. EPA). The induced blanket reactor has achieved 80 % reduction of volatile solids.
Covered lagoon digesters and complete mix digesters differ in their methane production
characteristics, and energy conversion systems that rely on methane from anaerobic digesters should be
chosen according to the end-use objective for the system. Complete mix digesters may produce heat and
electricity at a constant rate throughout the year because heat recovery may be used to heat the digesters in
the winter. Covered lagoon digesters may consistently produce biogas only in months when the temperature
exceeds 39 °F (Figure 7.6). Reactors may be successful in the northern United States if careful attention is
paid to heat management. The facilities that are located in the southern portion of the country are usually
warm enough for cost-effective energy recovery from covered lagoon digesters. Complete mix digesters
may be used in cold or warm climates. If odor control is the only objective, either covered lagoon or
complete mix digesters may be used, but odor control will be less effective in the winter for covered lagoon
digesters in the south (McNeil Technologies, 2000).
Photo courtesy of USDA NRCS.
Figure 7.6. Covered manure tank generating methane in Iowa.
A review of recent dairy waste anaerobic digestion studies has established that most engineers
anticipate a 50 percent conversion of volatile solids to gas. The planned Three-Mile Farm (Oregon) dairy
waste thermophilic anaerobic digestion facility is expected to achieve a 50 percent volatile solids conversion
to gas. The C. Bar M. (Idaho) plug flow anaerobic digester facility anticipated a 50 percent conversion of
dairy waste volatile solids to gas. The recently completed Myrtle Point (Oregon) feasibility study utilizing
the gravity separation contact process anticipated a 50 percent conversion of dairy waste volatile solids to
gas. Relatively high loading rates were anticipated in each case. The organic loading rates varied between
5.6 and 6.4 kg/m3/d (Burke, 2001).
7.5 Technologies Requiring Significant Additional Research Before Implementation-Aerobic
7.5.1 Aerobic Digestion
The use of aerobic digestion to treat livestock wastes was born out of a need to reduce the pollution
of both surface and ground water supplies, which had been caused by the spreading of manures, and the
unavailability of land during much of the year for immediate spreading of animal wastes. For these reasons,
farmers began to look for a low-cost, manure storage method that would not give rise to intolerable odors
and insect breeding (U.S. EPA, 1972).
One of the simplest methods of low odor waste treatment is the aerobic biological treatment process.
Aerobic treatment for the removal of biodegradable organic matter from liquid wastes is an odorless process
and consists of two phases operating simultaneously. One phase is biological oxidation that has by-products
such as carbon dioxide and water. The second phase utilizes the energy from the oxidation phase for
synthesis of new cells (U.S. EPA, 1972). The degree of oxidation depends on the amount of oxygen
provided, the reaction time allowed in the treatment process, and temperature. The relatively strong
oxidizing environment leads to a more extensive breakdown of organic compounds, with water, carbon
dioxide, nitrates, sulfates, and other simple molecules being the products (Bicudo, 2001). With
conventional aerobic digestion, substantial reductions in total and volatile solids, biochemical and chemical
oxygen demand, and organic N may be realized.
An aeration basin typically is used for the aerobic digestion of municipal and industrial wastewater
biosolids. In contrast, several reactor types, including oxidation ditches and mechanically aerated lagoons,
as well as aeration basins, have been used for the aerobic digestion of animal manures. Under commercial
conditions, the oxidation ditch has been the most commonly used because it may be located in the animal
housing unit under cages for laying hens or under slatted floors for swine (U.S. EPA, 2001).
220.127.116.11 Types of Aerobic Digestion Technologies
18.104.22.168.1 Oxidation Ponds
The oxidation pond (naturally aerated lagoon) is a shallow pond that uses a natural system of
evaporation as a means of effluent reduction. In an aerobic lagoon or oxidation pond, there must be an
abundance of dissolved oxygen available in the water for the aerobic bacterial and other organisms to
interact in the biochemical process that decomposes or breaks down the organic materials in the liquid
waste. Normally, aerobic lagoons range from 3 to 5 feet deep. If oxidation ponds are properly constructed
and hold the wastes for a sufficient time, a good destruction of coliform organisms and a satisfactory
reduction of BODs occur. The effluent is usually high in dissolved oxygen (U.S. EPA, 1972). The main
advantages of aerated lagoons are that aerobic digestion tends to be more complete and it produces fewer
odors than anaerobic digestion (McNeil Technologies, 2000).
Because of the large surface area required, oxidation ponds have not found favor with livestock
producers. Vast amounts of land are required - as much as 25 times more surface area and 10 times more
volume than an anaerobic lagoon 10 feet deep. Thus, naturally aerobic lagoons are impractical for primary
oxidation and are generally not recommended for treatment of livestock production wastes (Barker, 1996).
Their use has been essentially limited to receiving effluent from anaerobic lagoons and other treatment
22.214.171.124.2 Mechanically Aerated Lagoons
A mechanically aerated lagoon is similar to a stabilization pond except that it is equipped with one
or more electrically powered aerators that treat effluent by mixing it with air (Water for the World).
Mechanically aerated lagoons combine the odor control advantages of aerobic digestion with relatively
small surface requirements. Aerators are used mainly to control odors in sensitive areas and for nitrogen
removal at limited land disposal sites (Barker, 1996). A major disadvantage of mechanically aerated
lagoons is the expense of continually operating electrically powered aerators. Larger anaerobic lagoons
may provide similar performance with less expense (Barker, 1996).
Conventional aerobic digestion is a process used frequently at small municipal and industrial
wastewater treatment plants for biosolids stabilization. Conventional aerobic digestion is an option for all
swine and poultry operations where manure is handled as a liquid or slurry. With proper process design and
operation, a 75 to 85 % reduction in BODs appears achievable, with a concurrent 45 to 55 % reduction in
COD, and a 20 to 40 % reduction in total solids. In addition, a 70 to 80 % reduction of the N in both poultry
and swine wastes via nitrification-denitrification also appears possible. Total P is not reduced, but the
soluble fraction may increase (U.S. EPA, 2001).
Unlike anaerobic digestion, aerobic digestion has not been adapted to any significant degree by the
poultry, dairy, or swine industries, although a number of research and demonstration scale studies were
conducted in the late 1960s and early 1970s. Problems related to process and facilities design, together with
the significant increase in electricity costs in the early to mid-1970s, led to a loss of interest in this animal
waste treatment alternative. It is possible that no aerobic digestion systems for animal wastes are currently
in operation in the poultry and swine industries.
126.96.36.199 Constructed Wetlands
Constructed wetlands (or treatment wetlands) are man-made, shallow ponds or channels that have
been planted with emergent aquatic plants, and are designed, built and operated specifically for wastewater
treatment. They rely upon natural microbial, biological, physical, and chemical processes to treat
wastewater. To allow optimum process control, water control structures such as gates, valves and dikes
have been engineered to control the flow direction, hydraulic retention time, and water level. They are
typically constructed with uniform depths and regular shapes near the source of the wastewater and often in
upland areas where no wetlands have historically existed. Constructed wetlands are regulated as wastewater
treatment facilities and may not be used for compensatory mitigation (USEPA, 2000b).
188.8.131.52 Restored Wetlands
Created or restored wetlands are designed, built (or restored), and operated primarily for wildlife
habitat and should not be confused with constructed wetlands. In an effort to mimic natural wetlands,
habitat wetlands often have a combination of features such as varying water depths, open water and dense
vegetation zones, vegetation types ranging from submerged aquatic plants to shrubs and trees, nesting
islands, and irregular shorelines. They are frequently built in or near places that have historically had
wetlands and are often built as compensatory mitigation. Created and restored wetlands are generally
inappropriate for CAFO applications and are not discussed further.
184.108.40.206 Enhancement Wetlands
Enhancement wetlands are constructed wetlands providing polishing (advanced or tertiary treatment)
of wastewater that has been extensively pre-treated, usually to secondary treatment standards. They are
often designed, built, and operated for both wastewater treatment and other functions, such as wildlife
habitat, outdoor classrooms, or recreational areas. While there may be applications for enhancement
wetlands as a tertiary treatment process in certain circumstances, they are generally inappropriate for CAFO
applications and are not discussed further.
220.127.116.11 Free Water Surface (FWS) Wetlands
Constructed wetlands have been classified in the literature and by practitioners into two types. Free
water surface (FWS) wetlands, also known as surface flow (SF) wetlands, resemble natural wetlands in
appearance because they contain aquatic plants that are rooted in a soil layer on the bottom of the wetland,
and water flows through the leaves and stems of plants (Figure 7.7).
microbes on stem
Figure 7.7. Free Water Surface (FWS) Wetland.
18.104.22.168 Vegetated Submerged Bed (VSB) Wetlands
Vegetated submerged bed (VSB) systems, also known as subsurface flow (SSF) wetlands, do not
resemble natural wetlands because they have no standing water (Figure 7.8). They contain beds of media
such as crushed rock, small stones, gravel, sand, or soil that has been planted with aquatic plants. When
properly designed and operated, wastewater stays beneath the surface of the media, flows in contact with the
roots and rhizomes of the plants, and is not visible or available to wildlife.
22.214.171.124 Reciprocating (ReCip) wetlands and vertical-flow (VF) wetlands
Reciprocating (ReCip) wetlands and vertical-flow (VF) wetlands are modifications of the VSB
process. ReCip wetlands reciprocate flow back and forth between two VSBs in parallel in a way that allows
the VSBs to alternate between saturated (anaerobic) and unsaturated (aerobic) conditions (Behrends, et al.,
1996). VF wetlands are similar in design and operation to typical vertical flow, intermittent or recirculating
sand or gravel filters, which have been planted with aquatic plants.
7.5.3 Treatment Mechanisms
The primary pollutant removal mechanisms for BOD5 and solids (TSS) are physical removal and
biodegradation. Physical mechanisms include impingement on plant or media surfaces, entrapment in plant
parts or media, and sedimentation. All of these mechanisms are enhanced by the tortuous flow paths and
quiescent hydraulic conditions found in wetlands. Once materials are removed from the water column by
physical mechanisms, biodegradation occurs. Obligate and facultative anaerobic conditions predominate in
VSBs and FWS wetlands, while the operating characteristics of ReCip and VF wetlands promote alternating
anaerobic and aerobic conditions.
roots and media
Figure 7.8. Vegetated Submerged Bed (VSB) Wetland.
For CAFO wastewaters (high BOD5 and ammonia concentrations) in VSBs and FWS wetlands
(shallow depths and large surface areas), ammonia volatilization may be a significant removal mechanism
for nitrogen, especially in warmer climates. Wastewater lagoon studies indicate that nitrogen losses up to
95% may occur under ideal conditions, with ammonia volatilization being the dominant mechanism (Reed,
etal., 1995). However, research is needed to verify this mechanism in constructed wetlands. Microbial
nitrification/denitrification as a nitrogen removal mechanism in VSBs and FWS wetlands is less likely,
because of the predominance of anaerobic conditions. Nitrification of ammonia is unlikely to occur in
VSBs and will occur in the FWS wetlands only if adequate open water zones are incorporated into the
design (USEPA, 2000a).
Phosphorus removal in all types of constructed wetlands is primarily limited to adsorption to solids.
The adsorbing solids may be material in the influent wastewater, which has been removed from the water
column, plant detritus, or the soil or media in the wetland. All of these materials have a finite adsorption
capacity, so phosphorus removal may occur for a time when a constructed wetland begins operation, but
removal will decrease or stop as adsorption sites are filled. Long term phosphorus removal will be limited
to phosphorus that adsorbs to new material entering the wetland that is buried before the phosphorus may be
released back into the water column (Kadlec and Knight, 1996). Because new regulations will likely make
phosphorus the limiting factor for land application of wastewater (USEPA, 2001), an additional unit process
to remove phosphorus will be required.
7.5.4 Plant Functions
The role of aquatic plants in the treatment process is still not clearly understood but appears to be
limited primarily to providing an attachment surface for microbes in FWS wetlands. While emergent
aquatic plants may provide oxygen from the atmosphere to their roots, field experience has shown that the
small amount of oxygen that may "leak" from plant roots is insignificant compared to the organic and
nitrification oxygen demands of heavily polluted wastewater applied at practical loading rates.
Nutrient utilization by plants is less than 20% of influent values for heavily polluted wastewaters
(Reed, et al,1995) even if the plants are routinely harvested. If plants are not harvested, plant utilization is
largely negated when the plants die in the fall and winter. Unless plant material containing nutrients is
buried in the sediments before the nutrients leach out as the plants decompose, the nutrients will return to
the water column.
Submerged aquatic plants in open water areas of FWS wetlands may supply oxygen to the
wastewater during daylight hours. While they have been used in wetlands treating municipal wastewater,
research is needed to determine their ability to tolerate heavily polluted CAFO wastewater. Floating aquatic
plant systems (e.g. duckweed, water hyacinths, and algae) have been used to treat a variety of wastewaters.
However, these systems require constant removal of plants and handling of the harvested material. While
the harvested material may be processed and used as feed or land applied, very few operations using floating
plants have succeeded in the U.S.
Researchers have hypothesized other plant functions in treatment wetlands. Plant detritus may
provide carbon for microbial reactions and enzymes exuded by plant roots may enhance degradation of
some organic compounds. Certain plant species may have symbiotic relationships with beneficial microbes
attached to their roots, and these relationships could be useful for treatment purposes if they can be defined.
Not enough research has been conducted to validate any of these functions.
7.5.5 Risk Associated with Constructed Wetlands
The use of constructed wetlands as a treatment technology carries some degree of risk for several
reasons. First, although there is no evidence of harm to wildlife using constructed wetlands, some
regulators have expressed concern about constructing a system that will treat wastewater while it attracts
wildlife. Unfortunately, there has not been any significant research conducted on the risks to wildlife using
constructed wetlands. Although they are a distinctly different type of habitat, lagoon treatment systems
have not shown evidence of harm to wildlife. The fact that lagoon systems have been in use for many years
suggests that there may not be a serious risk for wetlands treating agricultural wastewater. Of course, if a
wetland is going to treat wastewater with high concentrations of known toxic compounds, the designer will
need to use a VSB system or incorporate features in an FWS wetland that restrict access to wildlife.
Second, although many texts and design guidelines have been published for constructed wetlands in
the past 10 years (Kadlec and Knight, 1996; Payne Engineering and CH2M-H111, 1997; Reed, et al., 1998;
USD A, 1991; USD A, 1995; USEPA, 2000a), questions remain about their application, design, and
performance. Constructed wetlands are complex systems in terms of biology, hydraulics, and water
chemistry. There is a lack of quality data of sufficient detail, both temporally and spatially, on full-scale
constructed wetlands, forcing modelers and designers to derive design parameters by aggregating
performance data from a variety of wetlands, which leads to uncertainties about the validity of the
parameters. The design process is still empirical, that is, based upon observational data rather than scientific
theories. Due to the variability of many factors at constructed wetlands that have been observed by
researchers (e.g., climatic effects, influent wastewater characteristics, design configurations, construction
techniques, operating parameters, and maintenance practices), there will continue to be disagreement about
some design and performance issues for some period of time.
Third, there are several common misconceptions about constructed wetlands. Some people think
that VSBs and FWS wetlands are aerobic systems, or at least have many aerobic microsites. As noted in the
previous discussion of plants, this is not true. Another myth is that constructed wetlands remove large
amounts of nutrients. As discussed previously, although some nutrient removal does occur, it is not at the
high levels reported in some early research.
Finally, as noted in a review of constructed wetlands for wastewater treatment by Cole (1998),
constructed wetlands are not uniformly accepted by all state regulators or EPA regions. Some authorities
encourage the use of constructed wetlands as a proven treatment technology. Others still consider them to
be an emerging technology due in part to concerns about the issues discussed above. As with any new
treatment technology, uniform acceptance of constructed wetlands will take some time.
7.5.6 Application and Performance of Constructed Wetlands for Agricultural Wastewaters
Although an operation in Iowa has used a constructed wetland since the 1930's, constructed wetlands
have been more commonly used to treat agricultural wastewaters in the United States for about 10 years.
The USDA-NRCS issued guidance on constructed wetlands for agricultural wastewater treatment in 1991
(USD A, 1991). The U.S. EPA's Gulf of Mexico Program funded a project to assess the use of constructed
wetlands for CAFO wastewater in the late 1990's (CH2M-Hill, 1997; Payne Engineering and CH2M-Hill,
1997; Knight, et al., 2000). The study depended primarily on data from a subset of the North American
Treatment Wetland Database, v 2.0 (NADB) (USEPA, 1999) and summarized the performance of wetland
systems (Table 7.3).
Table 7.3. Performance Data Summarized for Gulf of Mexico Program (CH2M-Hill, 1997)
Total Nitrogen (TN)
Total Phosphorus (TP)
The entire NADB lists 135 wetland treatment systems at 69 sites that use constructed wetlands to
treat agricultural wastewaters (Table 7.4).
Table 7.4. Agricultural Treatment Wetlands in the NADB
The wetlands are located in 18 states throughout the United States and in 5 Canadian provinces. A
wide variety of plant species have been used, but cattails (Typha), grasses/reeds (e.g. Phragmites), and
sedges/rushes (e.g. bulrush (Scirpus)) were the predominant plants in 48%, 28%, and 14% of the systems,
respectively. Floating plants, such as duckweed (Lemna)., were predominant in 4% of the systems. The
wetlands range from experimental systems at research farms to full-scale systems, so their size and costs
vary greatly (Table 7.5). Because of the wide variation, the size and cost listed cannot be used for design
Table 7.5. Range of Costs and Operating Parameters for NADB Agricultural Treatment Wetlands
Area (per AUJ)
Cost (per Area)
Cost (per Flow)
Cost (per AU)
Number of systems in the NADB with data (out of the total of 135 systems)
Actual flows were usually less
General treatment performance for several common wastewater parameters, shown as the 95%
confidence interval about the mean, calculated from the NADB, is shown in Table 7.6. Because these are
overall average values from all of the systems, regardless of size, flow or type of wastewater, the values
shown cannot be used for design purposes. However, the numbers do give a general impression of the
capabilities of constructed wetlands for treating CAFO wastewater. While it is obvious that effluent from
these systems cannot be discharged to surface waters, the reductions are substantial and yield higher quality
water for land application.
Table 7.6. 95% Confidence Interval about the Mean for all NADB Agricultural Treatment Wetlands
246 - 352 mg/L
501 -956 mg/L
141 -174 mg/L
24 - 29 mg/L
2.1 -2.7 mg/L
2 x 105 - 4 x 105
99 - 136 mg/L
360 - 676 mg/L
79 - 102 mg/L
15 - 18 mg/L
1.4 -2.0 mg/L
2 x 104 - 5 x 104
34% - 44%
18% - 35%
0.8 -1.0 log
Figure 7.9 shows a hog operation with a lagoon flowing into a constructed wetland. The treatment
efficiency is reported to yield an effluent of higher quality than a nearby municipal wastewater treatment
plant. Figure 7.10 shows a ground level view of the wetland with the owner making observations for his
Photo courtesy of USDA NRCS.
Figure 7.9. View of a hog operation with a lagoon flowing into constructed wetlands for treatment of wastewater.
Photo courtesy of USDA NRCS.
Figure 7.10. Ground level view of constructed wetland with the owner making observations for his records.
The USEPA currently has an agreement with the Tennessee Valley Authority to evaluate the use of
its ReCip system at a swine operation in Alabama. The system treats wastewater from the anaerobic lagoon
that receives the flush water from the swine buildings. The preliminary results from the first year of
operation are shown in Table 7.7. As expected from a system with alternating aerobic and anaerobic
conditions, the ReCip systems had good BOD5 and ammonia removal. Also as expected for any wetland
system, phosphorus removal decreased from an initial 90% removal efficiency (< 10 mg/L in the effluent) to
20% removal (40 mg/L in the effluent) during the one year of operation.
Table 7.7. Preliminary Averages from ReCip System Treating Swine Wastewater
2 logic units
7.5.7 Processes to Significantly Reduce Pathogens (PSRP)
Manure should be treated to effectively eliminate pathogens and applied appropriately to minimize
the possibility of pathogen survival and subsequent crop contamination (IFT, 2002). An indication of the
level of concern that World Health Organization (WHO), U.S. EPA, and the State of California place on the
issue of proper application of recyclable materials to land is shown in Table 7.8 which presents
microbiological quality guidelines and standards for the application of wastewaters to land. A PSRP is a
technology that is broadly defined as one that reduces both the pathogen load and vector attraction in the
environment (U.S. EPA, 1989). Typically, the pathogen reduction is a minimum of one order of magnitude.
Many factors may induce pathogen reduction occurring with various treatments such as temperature,
storage length, and continuous addition of manure. Presently, facultative lagoons and composting are mostly
used to manage waste at CAFOs. Likely, some pathogen reduction occurs, but it is difficult to quantify the
amount. The methods that may be used in an animal feeding operation to treat manure and reduce pathogens
include: composting; aerobic digestion, high temperature; anaerobic digestion at different temperatures;
combinations of aerobic and anaerobic digestion; and long term storage of manure before land application.
Implement control technologies for treatment of animal waste to reduce pathogen loads prior to land
application or off-site transfer. Based on review of the peer-reviewed scientific literature, and using best
professional judgment, it is recommended to take steps now to reduce potential exposures to pathogens via
this route. Several technologies have demonstrated the capability to significantly reduce the risk of pathogen
contamination from land application of animal waste. The technologies also reduce the viability of
Cryptosporidium oocysts, which have been found to be difficult to treat by publicly owned treatment works.
These technologies are listed below.
Using either the within-vessel, static aerated pile or windrow-composting methods, the temperature
of the animal wastes/manure is raised to 40°C (104°F) or higher and remains at 40°C (104°F) or higher for
five days. For 4 hours during the 5-day period, the temperature in the compost pile exceeds 55°C (131°F)
(U.S. EPA, 1989).
Table 7.8. Microbiological Quality Guidelines & Standards For Application Of Wastes To Land
Calif. Code of
Calif. Code of
Crops likely to be
Pasture, fodder &
Crops likely to be
of pasture, fodder
A sewage sludge
municipal Class B
Land discharge of
Irrigation of food
Irrigation of dairy
< 1 helminth
< 1,000/100 ml
< 1,000/100 ml
< 100,000/100 ml
<l,000/g total solids
solids (dry weight)
< 14/100 ml)
< 2.2/100 mlb
< 23/100 mlb
< 1 PFU/4g
(a) NR = No standard recommended
(b) Standard for fecal or total coliforms
126.96.36.199 Air Drying
Animal wastes/manure is dried on sand beds or on paved or unpaved basins. The animal
wastes/manure dries for a minimum of three months. During 2 of the 3 months, the ambient average daily
temperature is above 0°C (32°F).
188.8.131.52 Facultative lagoons / Storage
Animal waste/manure is treated or stored in a lagoon system at a temperature of < 5°C for a period
of at least six months or at a temperature of > 5°C for a period of at least four months. Since all wastes
must be in a lagoon for the specified period, two lagoons will likely be needed such that while one is filling,
the other may be aging. This avoids short-circuiting.
184.108.40.206 Anaerobic Digestion
Animal waste/manure is treated in the absence of air for a specific mean cell residence time (i.e.,
solids retention time) at a specific temperature. Values for the mean cell residence time and temperature
must be between 15 days at 35°C (95°F) to 55°C (131°F) and 60 days at 20°C (68°F) (U.S. EPA, 1989).
220.127.116.11 Aerobic Digestion
Animal waste/manure is agitated with air or oxygen to maintain aerobic conditions for a specific
mean cell residence time (i.e., solids retention time) at a specific temperature. Values for the mean cell
residence time and temperature must be between 40 days at 20°C (68°F) and 60 days at 15°C (59°F) (U.S.
18.104.22.168 Lime Stabilization
Sufficient lime is added to the animal waste/manure to raise its pH to 12 for > two hours of contact.
*More detailed information on Technologies 1, 2, 4, 5, and 6 in Environmental Regulations and Techno-
logy: Control of Pathogens and Vector Attraction in Sewage Sludge (EPA/625/R-92/013 - 1999 Edition.)
Table 7.9 shows technologies for potential use at CAFOs and their expected effect on pathogen
levels (USEPA, 2001).
Table 7.9. Effects of waste treatment and management systems on pathogen reductions.1
Anaerobic thermophilic digesters
Anaerobic mesophilic digesters
Aerobic (liquid fraction)
Chemical (liquid fraction)
Alkaline treatment (liquid or dry)
99.0% per cell
99.0% per cell
99.0% per cell
swine, dairy, beef, layers
swine, dairy, beef
swine, dairy, beef
swine, dairy, beef
swine, dairy, beef
swine, dairy, beef
swine, dairy, beef
swine, dairy, beef
residence time of months
residence time of months
Do not work well with
high solids content,
Time- and temperature -
Time- and temperature-
Time- and temperature-
need mixing for aeration
Nummary from USD A/EPA "Workshop on Emerging Infectious Disease Agents and Issues Associated with Animal Manures,
Biosolids, and Other Similar Byproducts" June 4-6, 2001 Cincinnati, OH. (Reference in bibliography section)
2Maximum pathogen reductions converted from Iog10 reductions (1 Iog10 reduction = 90.0%, 2 Iog10 reduction = 99.0%, 3 Iog10
reduction = 99.9%).
Most technologies currently or likely to be used by CAFOs reduce pathogen levels up to 99%.
Several factors may impair the pathogen reduction obtained with these technologies. Most of these
technologies are time-dependent (some requiring months of residence time) and pathogen reduction may be
lower with reduced residence time. Some of these technologies operate under conditions of continuous
addition of manure, which may impede pathogen reduction. Some of the technologies like constructed
wetlands and composting operate optimally under specific solids level ranges (percentage) and could have
poor pathogen reductions outside those optimums. Several of these technologies (anaerobic thermophilic
digesters, constructed wetlands, and thermal processes) operate optimally under specific temperature ranges
and could have impaired pathogen reductions outside those optimums.
7.6 Land reclamation
7.6.1 Non-Farm Land Applications
In large parts of the United States areas exist where untreated or semi-treated manures may be
land-applied with little risk of pathogens reaching human receptors directly. These areas will allow aerobic
degradation and provide a use for carbon and nitrogen in the materials. The needed research builds on the
information learned from farm applications of feedlot waste, and extends it to new markets for the material.
The main limitations to current off-site use of these materials are lack of information about the effects and
economics of transportation.
There are two categories of non-farm land applications of CAFO wastes: on-site and off-site. On-
site application could include CAFO controlled forest plots and wetlands, or perhaps a combination of trees,
cropland, and wetland. Feed lot wastes could possibly be safely used on off-site applications, various land
reclamation projects, forest crops, and on vegetation in uninhabited areas such as along highways.
Hard rock and coal mines have left sterile scars across thousands of square miles of landscapes in
this country's mining regions, frequently covering topsoil layers with infertile subsoil, rock, and mine
tailings. These are unsightly, have no habitat value, and often acidify rainwater causing downstream
damage. Restoring these sites requires carefully reconstructing the conditions for pedogenesis, or soil
creation. Organic material must be incorporated to establish vegetation, and annual or more frequent
applications may aid in ensuring successful establishment of the conditions for sustainable vegetation.
Similarly, restoration of coal mine sites may benefit from application of lime and organic material in the
form of animal waste. Heavily eroded lands may also benefit from application of manure combined with
dredge spoil as a step towards recreation of the soil surface.
7.6.2 Phytoremediation Projects, Sediment Recycling, and Landfill Covers
Small sites, ranging in the tens of acres, exist across the United States in locations that could
potentially accommodate applications of CAFO materials several times per year. These sites are typically
secure from casual human intrusion, and the plants grown on them are not consumed by people nor by
livestock. Generally these sites pay for fertilizer and organic material, especially during initial installation,
which could offset some transportation costs.
7.6.3 Riparian Corridors
Riparian corridors are stream bank and riverside strips of trees and other vegetation that separate
agricultural fields from surface water and protect that water by filtering, degrading, and using excess
fertilizer, herbicide, and pesticide. This run-off prevention system may be extremely effective both at
improving stream cleanliness and at providing enhanced habitat for both terrestrial and aquatic species.
Thousands of miles of riparian corridors have been planted and are continuing to be planted around the
Chesapeake Bay and along the Mississippi watershed.
7.6.4 Forest Products: Short Rotation Wood Crops- Pulp & Paper, Lumber, Fuel
The wood products industry plants tens of thousands of acres of fast growing hybrid trees each year.
These trees thrive on high nutrient levels. Regular applications of feedlot waste might be an ideal use if the
transportation and safety considerations may be satisfactorily explored. Forest application of treated sewage
sludge has been researched, and that work might be applicable to some extent.
7.6.5 Highways: Roadsides and Medians
The thousands of miles of grassy medians and roadsides present an opportunity for beneficial
disposal of CAFO materials. Regular, thin applications of liquid or solid material could provide a safe area
for aerobic degradation, distant from human contact, on plants not intended for livestock consumption.
Each of these areas has needs and concerns that should be researched before application. There
should be an estimate of how many acres or square miles are available of each type of terrain in various
geographic regions. Different regions have different usage opportunities; for example, Appalachia and the
Rocky Mountains need organic material for hard rock mine reclamation, while the Great Lakes area have
dredged sediments that need organic materials to encourage contaminant degradation and plant growth in
order to turn dredged material into soil suitable for beneficial reuse.
Finally the loading rate limitation for each terrain and application needs to be determined. The
quantity of waste that may be safely applied to a particular project depends on the form of the waste (solid
or liquid), the nutrient and chemical load of the material, and the capacity of the application to hold and
utilize the material. That capacity is, in turn, based on equipment limitations, nutrient use capacity of the
particular vegetation, seasonal access to sites, and climate considerations. Each use would require research
and experimentation to determine the type of equipment that would be needed for application in the target
A protocol that outlines how to match resources (waste sources) with utilizers within an economical
travel distance would be extremely useful. Such a guide would help local feedlot farmers, foresters,
ecological restorers and others answer those questions that prevent the synergies that allow use of this
material as a resource.
8 Research Needs Associated with CAFOs
Identified research needs related to CAFO issues fall into several categories. The categories are
interactive and mutually supporting. One category is stressor evaluation and quantification. A second
category is method development; new methods are needed to rapidly and inexpensively measure stressor
levels. New methods are also needed to identify sources of stressors in the environment. A third research
category encompasses process research. Process research will involve several levels of work from bench-
scale to field-scale. How may waste treatment systems be optimized for control of different stressors? How
may they be made cost effective? Can salable products be generated from waste streams? Different
stressors will have to be addressed individually and in combination. The fourth category of research needs
relates to stressors in the environment. Fate and effects of specific stressors must be elucidated.
Management practice effects on stressors must be studied. Transport of stressors in different media from
sources to receptors must be understood. Other topics of research that are presented in more detail are
ground water research, aerosol research, and land reclamation.
8.2 Stressor Evaluation and Quantification
The first two research categories are closely related. Stressor evaluation and quantification is a
fundamental need in identifying problem areas. Current methods are quite good for measuring nutrient
levels in various media. Methods for sediments in water are also good. Source identification for nutrients is
more of a problem. In some cases, isotope analysis of C, N, and P could lead to identification of sources of
stressors. Much work needs to be done to make isotope methods more readily applicable. Quantitative
analysis of antibiotics, EDCs, and pathogenic microorganisms in waters, soils, sediments, and manures is
needed to evaluate stressor content and movement. Rapid, precise methods need to be developed for
analysis of these stressors in the different matrices. Methods for analysis of EDCs and antibiotics in
different matrices will ultimately rely on GC-MS and HPLC-MS for quantification. Analysis of pathogenic
organisms will require a completely new approach. Currently, fecal coliforms (FC) and fecal streptococci
(FS) are used as indicators of fecal pollution. There may easily be cases where pathogenic organisms may
exist with no associated FC or FS. The best approach requires developing methods that may be applied to
water, soil, sediment, or manure to directly detect and quantify specific pathogens.
The organisms most commonly implicated in human illness should be included in the test method.
Among the organisms of concern are E. coli O157:H7, Salmonella spp., Campylobacterjejuni, Listeria
monocytogenes, Leptospirillum spp., Cryptosporidiumparvum, and Giardia lamblia. These bacterial
pathogens are perhaps the most readily detected and most commonly implicated in causing health problems.
With the advent of genetic analysis methods, it is possible to develop means to specifically identify
organisms and track them to their source. Work has been done on source identification with some
organisms in agricultural areas of Oregon and California. Protozoan parasite detection and enumeration is
much more difficult. Currently, the methods require large sample volumes, are laborious, and require
highly skilled analysts. Development of rapid methods for identification and enumeration of protozoan
parasites is highly desirable.
Associated with the need for microbiological methods is the need to determine the survival of known
pathogens under different conditions. Treatment or storage of manures should have effects on microbial
populations. These effects should be determined to establish the utility of different treatment systems for
reducing pathogen loads. Detection and enumeration methods for the different organisms are required to
address this need. Compilation of a database of microbiological information is needed to assess and track
epidemiological information related to pathogens in animal waste. Little of this information is readily
available. Similarly, the database should include animal disease epidemiological data as well. Existing
literature on baseline mortality of animals needs to be compiled as well. The potential financial loss from
an outbreak of animal pathogens is on the order of several billion dollars.
8.3 Process Research
The third major category of research needed to address the environmental challenges of CAFOs is
process research. Process research entails examination of waste handling in the different sectors of
agriculture. Different treatment processes are effective in controlling different stressors. Waste treatment
processes with potential application to animal waste include lagoon storage and lagoon modification,
aerobic digestion, anaerobic digestion, staged aerobic/anaerobic digestion, thermophilic digestion,
composting, and lime treatment. Much work is needed to optimize these systems for controlling the
different stressors. Conditions of treatment that control nutrients may have little effect on pathogen survival
or may even encourage regrowth.
Stabilization of nutrients by alum is a new area of research. The use of alum on poultry litter has
shown greater promise in stabilizing P to prevent its runoff to surface waters and leaching to ground waters.
Alum also stabilizes ammonia, making poultry litter more valuable as a fertilizer. Conditions that control
pathogenic organisms may have little effect on nutrients. The different systems must be optimized for waste
type, stressor reduction and cost.
Another aspect for cost control is configuring treatment systems to generate salable products.
Anaerobic systems offer the possibility of CH4 production. Some processes may recover fertilizer elements
in condensed forms that are more readily salable. Methane may potentially provide energy for operation on
the farm. As a lower cost alternative, composting is a useful treatment alternative. Establishing
performance characteristics for different animal wastes and effects on different stressors is an important
goal. Performance of poorly practiced composting must be established with regard to stressor control.
While the major effort will focus on systems for larger CAFOs, the smaller producer should have
alternatives for waste handling available. Smaller systems should be developed to address the same
problems for the smaller producer. A complete systems approach will be needed to optimize nutrient
control, pathogen control, and value recovery.
8.4 Fate and Effects of Stressors in the Environment
The fate and effects of stressors in the environment and the transport of those stressors in the
environment generate questions that are difficult to answer. Land application is a major practice for the
disposal of animal wastes from large and small facilities. The effectiveness of buffer strips with different
types of vegetation, width, and interaction with other soil management procedures should be evaluated.
Related to land application is the control of sediment generation from application sites and CAFO facilities
themselves. Study of engineered structures to collect sediments and management techniques is needed with
regard to other stressors that may move with sediments. Sediments offer attachment sites for nutrients,
EDCs, and pathogens. How effective is reducing sediment movement in reducing other stressor movement
Another water management tool proposed to be useful in waste management is the constructed
wetland. How do constructed wetlands perform over long term use under different climatic conditions?
Are they efficient in solid/liquid separation? What functions do different aquatic plants carry out? How are
they best monitored for performance? Do they function to remove excess phosphorus? What air emissions
may be expected from different types of wetlands?
8.5 Ground Water
Future research related to CAFO impact on ground water may be categorized into the following
broad areas: 1) transport and fate; 2) hydrogeology; 3) testing and monitoring; 4) risk management; 5)
prevention; 6) predictive modeling; and 7) impact of CAFOs on ground water resources. Improved
knowledge of the major factors affecting nutrient transformation, transport, and reactions in ground water is
an area that requires attention by soil/environmental scientists, hydrologists, hydrogeologists, and
environmental engineers. Research is needed to understand the fate of nitrogen under aerobic and anaerobic
conditions (nitrate, ammonium, organic-nitrogen) in stream riparian buffers, wetlands, and hyporheic zones
(i.e., groundwater-surf ace water interface). Transport of nitrate by preferential flow from treated
soil/storage ponds to ground water and/or tile drains is a critical area of research. Research documenting
phosphorus losses from soil receiving manure via subsurface tile drainage is limited. Leaching of solutes
below earthen waste ponds/lagoons to deep ground water, where the primary mode of transport to ground
water is unsaturated flow, warrants further research. The mechanism of self-sealing, particularly the effect
of wetting/drying cycles on reducing the extent of sealing in lagoons is an area that needs further research.
A method needs to be developed to account for sealing effects and related factors, such as temperature,
waste characteristics, soil structure and texture, pond depth, and frequency of pump down.
The survivability and transport of manure pathogens in soil and aquifers is not well characterized,
especially transport mechanisms for Cryptosporidium oocysts in the subsurface. More studies and
information are needed on their movement in soils. Studies are needed to investigate the impact of periodic
freezing-thawing — a common phenomenon during United Kingdom winters particularly in upland sheep-
farming areas (ref?). Little research has focused on the role of plant roots and micro- and mesofauna in the
translocation of pathogens. The importance of preferential transport of microorganisms by macropores from
treated soils and/or leachate from earthen storage ponds warrants future research. Further investigation is
needed into the effectiveness of riparian buffers and wetlands for removal of pathogens from subsurface
water. Improved fundamental understanding of sorption/desorption characteristics and die-off rates of
microorganisms in different soils and aquifer sediments is essential in designing for and evaluating the
efficacy of alternative mitigating measures.
Continued research on fundamental understanding of movement of ground water (hydrogeology) in
unsaturated soil (vadose zone hydrology) is a major prerequisite for studying source and prevention issues.
Research is warranted to investigate seepage losses from storage pond side slopes subject to frequent water
level fluctuations. Technology is needed for measuring infiltration for low permeability soils. Further
research is warranted to compare evaporation from clear water and animal wastewater, which may affect
water balance in ponds and thus seepage losses.
Standardized methods are needed that may relate P quantity and intensity factors to desorption and
downward movement of P and thus to the potential for P loss in subsurface runoff; i.e., soil tests for
predicting potential for P loss in leaching and drainage waters. Soil monitoring methods to accurately track
nutrient leaching in soil to ground water warrants further research.
Operational research (e.g., systems analysis and optimization) and modeling are important research
areas, especially for risk management at the watershed scale. Because of uncertainty in seepage rates and
other environmental factors, effort should be directed toward the development of stochastic, risk-based
approaches for the design and performance evaluation of detention ponds/lagoons. Developing a reliable,
risk-based regulatory system that would be acceptable to regulators, operators, and the general public is a
future research need. Developing predictive models based on sound scientific principles for assessing the
impact of CAFOs on ground water and for risk-management in watersheds is an area of future research.
Preventing pollutants derived from animal waste from reaching ground water may result in
substantially reduced costs, otherwise incurred with treatment or removal of pollutants in drinking water.
This would require developing appropriate management practices for animal waste to reduce potential
groundwater pollution, e.g., by nitrate and pathogens. Methods need to be developed to evaluate the impact
of animal waste management practices at the individual, local level and at the integrated, watershed level.
Models are useful tools to identify sources and to estimate the relative loading of pollutants from
various management scenarios. Their role is best realized in complementing and not replacing
environmental monitoring. Rather than relying on costly intensive monitoring, simulation models may aid
in the development of cost-effective and optimal monitoring network. More effort is needed for modeling
pathogen transport and fate in the soil and groundwater. Models need to be revised to account for the
complex interactions governing movement of microorganisms and other pollutants in soils as well as in
micropores. Incorporating a macropore flow component may improve the performance of models to predict
the fate of injected animal manure. Because of uncertainty in seepage rates and factors governing
movement of pollutants (e.g., pathogens, nutrients, and salts), probabilistic/stochastic-based modeling
approaches will be needed for risk-based planning and decision making.
Evaluating the performance of alternative abatement measures will benefit from improving the
capability of current watershed models to simulate the capacity of riparian buffers, vegetative filtering
strips, detention reservoirs, natural/constructed wetlands, and tillage practices to reduce the impact of
manure from agriculture and runoff from storage facilities on water quality. Developing modeling systems
that integrate processes across watersheds (both surface and groundwater) warrants further research.
Integrating modeling technology with systems analysis will be needed for optimal selection of alternative
Future research may be needed to address the following institutional questions: At what level is risk
management conducted (individual home, farm, or community)? What strategies are used to control
groundwater contamination? How do we make decisions on whether to do community treatment versus
point-of-use treatment versus development of new water resources? Research is required to emphasize the
need to forge a working relationship among scientists, regulatory agencies, and stakeholders to develop
BMPs that are both environmentally sound and feasible in the short and long terms. Research is warranted
on the impact of socio-economic and political constraints on environmentally effective decision-making.
8.6 Aerosol Research
Aerosol issues form another field of work in the handling of CAFO waste. Often, the first
environmental impact of a CAFO is the odor generated by the animal waste. With the concentration of
large numbers of animals in smaller areas the potential for odor generation is high. The public may perceive
problems in such areas if the odors generated are irritating. Production of particulates from CAFOs is a
concern because the particulates may easily fall into the regulated size classes of PM2.5 or PM10. PM2.5
particles are respirable deep into the lung and may be a source of irritation or infection. Do particulates
carry intact microbial cells, endotoxins, and allergens? Can they be detected? Are there species-specific
aerosol patterns related to housing types and waste system types? Can housing systems be designed to
minimize particle generation? Odor impacts are largely subjective and difficult to measure objectively. Can
a classification system be created to make objective measures of odor problems? The system must be able
to identify and quantify odors with regard to duration, intensity, frequency and offensiveness. Are there
good emission rate models for ammonia, H2S, VOCs, and particulates? Are there ways to reduce emissions?
Ammonia falls into more than one group of problems because it has a strong odor, is a nutrient, and
may attach to particles. Volatile organic compounds also contribute to odor problems. Many of these
compounds are contained in manure and are created by microbial action during storage or digestion of the
manure. Can the processes used for waste handling be modified to reduce odor generating organic
compounds? Staged treatment processes may be able to reduce odor compounds concurrent with treating
the waste for other stressors. Would a biofilter be able to reduce odor compounds sufficiently to reduce the
impact of odors?
8.7 Land Reclamation
Reclamation of disturbed land is another possible use for animal waste. Many areas of the United
States have large tracts of land seriously disturbed by many causes. Strip-mined land, mine spoil banks,
seriously burned-over land, and new highway construction may create highly disturbed land. Much of the
soil replaced or exposed in these areas has little protection from further degradation from erosion and
supports poor plant growth. A potential use of animal manure is to create new soils by mixing manures with
excavated dredge spoil from waterways and application of the material to unproductive land. The manure
contributes organic matter and nutrients to the soil. Manure also conditions the soil to be more friable and
hold more water for plant growth. The amount of available land in different classes and the quantity of
manufactured soil that could be applied at one time must be determined. Another use for manufactured soil
is restoration of heavily eroded soil in the United States. Return of soil material to areas that have
experienced losses of topsoil could be a beneficial use of manure composted together with freshwater
dredge material from the large river systems in the United States. The U. S. Army Corps of Engineers
moves about 100 million tons of dredge material every year. Some of this material could be composted
together with manure to make a product that could replace eroded soils.
Agriculture and Agri-Food Canada. 1998. Hog Environmental Management Strategy/Situation
Analysis/Chapter 2/Environmental Issues. ManureNet/Hog Environmental Management Strategy Steering
Committee, pp. 1-5. Web Site:http://res2.agr.ca/initiatives/manurenet/en/hems/sit_anal_ch2.html.
AGSTAR Digest. 2003. Office of Air and Radiation, Unites States Environmental Protection Agency,
Washington, D.C. EPA-430-F-02-028.
Alonso, M. Lopez, 2000. The Effect of Pig Farming on Copper and Zinc Accumulation in Cattle in Galicia
(North-Western Spain). The Veterinary Journal. 160:259-266.
Al-Masri, M.R., "Changes in Biogas Production Due to Different Ratios of Some Animal and Agricultural
Wastes," Bioresource Technology, Vol. 77, Issue 1, March 2001, pp. 97-100.
Altekruse, S.F., M.L. Cohen, and D.L. Swerdlow. 1997. Emerging foodborne diseases. Emerg. Infect. Dis.
ASAE 1999. "Manure production and characteristics." AS Data: AS D384.1. American Society of
Agricultural Engineers, St. Joseph, Michigan
Atherton, F.C., Newman, P.S. et al 1995. An outbreak of waterborne cryptosporidiosis associated with a
public water supply in the UK. Epidemiol. Infect. 115:123-131.
Banton, Marcy I, et al. 1987. Copper toxicosis in cattle fed chicken litter. JAVMA, 191:827-828.
Barker, James C., "Lagoon Design and Management for Livestock Waste Treatment and Storage," North
Carolina Cooperative Extension Service, Water Quality & Waste Management, March, 1996.
http://www.baencsu.edu/programs/extension/publicat/wqwm/ebae 103 -83 .html
Baseline Reference of Feedlot Health and Health Management. Part II. 1999. USDA APHIS. Veterinary
Services. Centers for Epidemiology and Animal Health. 555 South Howes St. Ft. Collins, CO 80521.
Baseline Reference of Feedlot Management Practices. Part 11999. USDA APHIS. Veterinary Services.
Centers for Epidemiology and Animal Health. 555 South Howes St. Ft. Collins, CO 80521.
Baxter-Potter, W.R., and M.W. Gilliland, 1988. Bacterial pollution in runoff from agricultural lands. J.
Environ. Qual. 17:27-33.
Behm, Don (2), Date unknown, 111 Waters: The Fouling of Wisconsin's Lakes and Streams, The Milwaukee
Journal, Milwaukee, Wisconsin.
Behrends, L.L., F.J. Sikora, H.S. Coonrod, E. Bailey, andM.J. Bulls. 1996. Recipicrocating Subsurface-
flow Wetlands for Removing Ammonia, Nitrate, and Chemical Oxygen Demand: Potential for Treating
Domestic, Industrial and Agricultural Wastewater. Proceedings Water Environment Federation, 69th Annual
Conference, Dallas, TX, October 5-9, 1996. Vol. 5, pp. 215-263.
Bertoldi, M., Zucconi,F. and Civilini, M. 1988. Temperature, pathogen control and product quality.
Biocycle. Feb. 43-50.
Bicudo, Jose R., "Frequently Asked Questions about Aerobic Treatment," University of Minnesota
Extension Program, Biosystems and Agricultural Engineering.
http://www.bae.umn.edu/extens/faq/aerobicfaq.html. March 23,2001.
Bitzer, C.C. and J.T. Sims. 1988. Estimating the availability of nitrogen in poultry manure through
laboratory and field studies. J. Environ. Qual. 17: 47-54.
Blumenthal, U.J., Mara, D.D., Peasey, A., Ruiz-Palacios, G. and Stott, R. Guidelines for the microbiological
quality of treated wastewater used in agriculture: recommendations for revising WHO guidelines, Bull.
WHO, 78, 1104,2000.
Bohlke, J. K., and J. M. Denver. 1995. "Combined use of groundwater dating, chemical, and isotopic
analyses to resolve the history and fate of nitrate contamination in two agricultural watersheds, Atlantic
costal plain, Maryland." Water Resour. Res., 31, 2319-2339.
Bosch, DJ. and K.B. Napit. 1992. Economics of transporting poultry litter to achieve more effective use as
a fertilizer. J. Soil Water Cons. 47:342-346.
Brackett, R.E. 1999. Incidence and behavior ofListeria monocytogenes in products of plant origin. Pp. 631-
655. In E. T. Ryser and E. H. Marth (ed.). Listeria, listeriosis, and food safety. Marcel Dekker Inc., New
Burge, W.D., Miller, P.D. Enkiri,N.K. and Hussong,D. 1987. Regrowth of salmonella in composted sewage
California (State of). Wastewater reclamation criteria. California Code of Regulations, Title 22, Division 4,
Environmental Health, 1978.
Carne, S. R., P. W. Westerman, and M. R. Overcash. 1980. "Die-off of fecal organisms following land
application of poultry manure." J. Environ. Qua!., 9, 531-.
Chaney, Rufus, 2002. USDA. Telephone conversation with S. J. Stoll, 11/08/02.
Chaney, Rufus, 2000. Correspondence from R. Chaney to R. Alexander and participants in the Composting
Discussion, 2/5/00, www.mailman.cloudnet.com/pipermail/compost/2000-February/000765.html.
CH2M-Hill. 1997. Constructed Wetlands and Wastewater Management for Confined Animal Feeding
Operation. Pamphlet published by CH2M-Hill. (Available from Gulf of Mexico Program Public Information
Center, Stennis Space Center, MS, 601-688-7940.)
Choi K. 1999. Optimal operating parameters in the composting of swine manure with wastepaper. J-
Environ-Sci-Health,-Part-B,-Pestic-Food-Contam-Agric-Wastes 34, no. 6: 975-87.
Christie, P. and Beattie, J. A.M., 1989. Grassland soil microbial biommass and accumulation of potentially
toxic metals from long-term slurry application. J. Applied Ecology. 26:597-612.
Christen, K. 2001. Chickens, manure, and arsenic. Environmental Science & Technology, May 1, 2001.
Cieslak, Paul R., K.F. Gensheimer, et al., 1993. Eschericia coll 0157:H7 Infection from a Manured Garden,
The Lancet 1993; 342:367.
Ciravolo, T. G., D. C. Martins, D. L. Hallock, E. R. Collins Jr., E. T. Kornegay, and H. R. Thomas. 1979.
"Pollutant movement to shallow groundwater tables from anaerobic swine waste lagoons." J. Environ.
Qual, 8(1), 126-130.
Clausen, J. C., K. Guillard, C. M. Sigmund, and K. M. Dors. 2000. "Water quality changes from riparian
buffer restoration in Connecticut." J. Environ. Qual., 29(6), 1751-1761.
Cole, D.J., Hill, V.R., Humenik, FJ. and Sobsey, M.D. Health, safety, and environmental concerns of farm
animal waste, Occupational Medicine: State of the Art Reviews, 14, 423, 1999.
Compost Science and Utilization. 1993; 1 (2) 65-72.
Cook, M.G., P.G. Hunt, K.C. Stone, and J. H. Canterberry. 1996. Reducing diffuse pollution through
implementation of agricultural best management practices: a case study. Water Sci. Technol. 33:191-196.
Copeland, Claudia, and Zinn, Jeffrey, "Animal Waste Management and the Environment: Background for
Current Issues," National Council for Science and the Environment, CRS Issue Brief for Congress,
Washington, D.C., May, 1998
Cord-Ruwisch, Ralph, "Waste Not Too Hard to Digest," Murdoch News Article.
wwwcomm. murdoch. edu. au/web ster/A5 7. html.
Crandall, Christy A. 1999. "Distribution and fate of nitrate in shallow ground water of citrus farming areas,
Indian River, Martin, and St. Lucie Counties, Florida," in Effects of Animal Feeding Operations on Water
Resources and the Environment. Proceedings of the technical meetings, Fort Collins, Colorado, Aug. 30-
Sep. 1. US Geological Survey Open File Report 00-24.
Culley, J.L.B. and P. A. Phillips. 1982. Bacterial quality of surface and subsurface runoff from manured
sandy clay loam soil. J. Environ. Qual. 11:155-158.
Dalzell,H.W., A.J. Biddlestone, K.R. Gray, andK. Thurairajan. 1987. Soil Management: Compost
production and use tropical and subtropical environments. FAO Soils Bulletin 56, Food and Agriculture
Organization of the United Nations, Rome.
Dean, D. M., and M. E. Foran. 1992. "The effect of farm liquid waste application on tile drainage." J. Soil
Water Conserv., 47, 368-369.
De Lange, C. F. M., 2002. Effects of feeding strategy on growing-finishing pig performance and nutrient
excretion. Midwest Nutrition Conference. Sept. 4, 2002. Indianapolis, IA, USA.
De Lange, C. F. M. 1997. "Dietary Means to Reduce the Contributions of Pigs to Environmental
Pollution" From Proceedings of Swine Production and the Environment Seminar "Living With Your
Neighbours", March 26, 1997, Shakespeare, Ontario.
Deluca, T. H., and D. K. Deluca. 1997. "Composting for feedlot manure management and soil quality." J.
prodAgric., 10(2), 189-190.
Devito, K. J., D. Fitzgerald, A. R. Hill, and R. Aravena. 2000. "Nitrate dynamics in relation to lithology and
hydrologic flow path in a river riparian zone." J. Environ. Qual. 29, 1075-1084.
Dillaha, T.A., J.H. Sherrod, D. Lee, V.O. Shanholtz, S. Mostaghimi, and W.L. Magette. 1986. Use of
vegetative filter strips to minimize sediment and phosphorus losses from feedlots: phase 1. experimental
plot studies. VPI-VWRRC-Bull 151. Virginia Water Res. Res. Center. VPI, Blacksburg, VA.
Doran, J.W. and D.M. Linn. 1979. Bacteriological quality of runoff from pastureland. Appl. Environ.
Dougherty, M., editor. 1999. Field guide to on-farm composting., NRAES-114. Ithaca, N.Y: NRAES.
Doughherty, M., L.D. Geohring, and P. Wright. 1998. Liquid manure application systems design manual.
Northeast regional agricultural engineering service. Ithaca, NY
Edwards, D.R. and T.C. Daniel. 1992. Environmental impacts of on-farm poultry waste disposal-a review.
Bioresource Technol. 41:9-33.
Eghball, B. 2000. Nitrogen mineralization from field-applied beef cattle feedlot manure or compost. Soil
Sci. Soc. Am. J. 64:2024-2030.
Eneji, A. E., Honna, T., and Yamamoto, S., 2001. Manuring effect on rice grain yield and extractable trace
elements in soils. J. of PI ant Nutrition. 24:967-977.
Entry, J.A. and N. Farmer. 2001. Movement of coliform bacteria and nutrients in groundwater flowing
through basalt and sand aquifers. J. Environ. Qual. 30:1533-1539.
Epstein, E. 1993. Neighborhood and worker protection for composting facilities: issues and actions, p. 319-
338. In H.A.J. Hoitink and H.M. Keener (ed) Science and Engineering of Composting: Design,
Environmental, Microbiological and Utilization Aspects. Renaissance Publ., Worthington,OH.
Evans, R.O., P.W. Westerman, and M.R. Overcash. 1984. Subsurface drainage water quality from land
application of swine lagoon effluent. Trans. Amer. Soc. Agric. Eng. 27:473-480.
Fernandes, L., and M. Sartaj. 1997. Comparative study of static pile composting using natural, forced and
passive aeration methods. Compost-Science-and-Utilization 5, no. 4: 65-77'.
Finstein, M.S., and Hogan, J.A.1993. Integration of composting process microbiology, facility structure and
decision-making, p. 1-23. In H.A.J. Hoitink and H.M. Keener (ed) Science and Engineering of Composting:
Design, Environmental, Microbiological and Utilization Aspects.Renaissance Publ., Worthington,OH.
Flynn, R. P., and C. W. Wood. 1996. Temperature and chemical changes during composting of broiler litter.
Compost-Science-and-Utilization 4, no. 3: 62-70.
Follet, Ronald F. September 1995. "Fate and transport of nutrients: Nitrogen." Working Paper No. 7, U. S.
Department of Agriculture, Agricultural Research Services, Soil-Plant-Nutrient Research Unit, Fort Collins,
Frarey, L., L. Hauck, R. Jones, and N. Easterling. 1994. "Livestock and the environment: Watershed
solutions." Texas Institute for Applied Environmental Research (TIAER). Tarleton State University,
Fukushima, H., Hashizume, T., et al. Clinical experiences in Sakai City Hospital during the massive
outbreak of enterohemorrhagic E. coli O157:H7 infection in Sakai City, Japan 1996. Pediatrics
International 41:213-217. 1999.
Gagliardi, J.V. and J.S. Kerns. 2000. Leaching of Escherichia coli O157:H7 in diverse soils under various
agricultural management practices. Appl. Environ. Microbiol. 66:877-883.
Gangbazo, G., A.R. Pesent, G.M. Barnwett, J.P. Charuest, and D. Cluis. 1995. Water contamination by
ammonium nitrogen following the spreading of hog manure and mineral fertilizer. J. Environ. Qual.
Geldreich, E.E., Fox, K.R., et al 1992. Searching for a water supply connection in the Cabool, Missouri
Disease Outbreak of E. coli O157:H7. Water Research 26:1127-1137.
Geohring, L. D., P. E. Wright, T. S. Steenhuis, and M. F. Walter. 1999. "Fecal coliforms in tile drainage
effluent." ASAE Paper No. 99-2203, St. Joseph, MI.
Gerritse, R. G. 1977. "Phosphorus compounds in pig slurry and their retention in the soil. In: Utilization of
Manure by Land Spreading, Commission European Commun., London. Cited in U.S.EPA (1998)
Gettier, S. W., Martens, D. C., E. T. Kornegay, 1988. Corn response to six annual Cu-enriched pig manure
applications to three soils. Water, Air, and Soil Pollution. 40:409-418.
Giddens, J. and A.P. Barnett. 1980. Soil loss and microbiological quality of runoff from land treated with
poultry litter. J. Environ. Qual. 9:518-520.
Gilley, J.E. and B. Eghball. 1998. Runoff and erosion following field application of beef cattle manure and
compost. Trans. Am. Soc. Agric. Eng. 41:1289-1294.
Goodrich, Phillip, R., "Creating Fuel from Manure is a Hot Topic - Again," Minnesota/Wisconsin
Engineering Notes, http://www.bae.umn.edu/extens/ennotes/enspr01/fuel.htm. May 2001.
Gordeiko VA, Pushkareva VI. (1990) [Yersinia in the water of wells near an area of irrigation with the
effluents from a swine-breeding farm complex] [Article in Russian] Zh Mikrobiol Epidemiol Immunobiol
1990 Oct; (10):65-6
Grey, M. and Henry, C. 1999. Nutrient retention and release characteristics from municipal solid waste
compost. Compost Science and Utilization. 7(1)42-50.
Hallberg, G. R. 1987. "A Primer on groundwater and groundwater contamination." In Chautauqua
Groundwater Workshop for Extension Agents, Chautauqua Institution., Chautauqua, New York, May 7-9,
1986, Publication #48, Ed.: Aletha Rudd, 4-42.
Halverson, M. 2000. IV. Part of the Pig Really Does Fly. The Price We Pay For Corporate Hogs.
Institute for Agriculture and Trade Policy, pp. 1-8. Web Site: http://www.iatp.org/hofreport/sec4 r.html.
Ham, J. M. 1999. "Field evaluation of animal-waste lagoons: Seepage rates and subsurface nitrogen
transport," in Effects of Animal Feeding Operations on Water Resources and Environment. Proceedings of
the technical meetings, Fort Collins, Colorado, Aug. 30 - Sep. 1. US Geological Survey Open-File Report
Hansen R.C., Keener Harold M., Dick W.A., Marugg C., and Hoitink Harry AJ. 1990. Poultry manure
composting. Ammonia capture and aeration control. In Pap-Am-Soc-Agric-Eng, No. 90-4062, 19 pp. St.
Joseph, Mich: American Society of Agricultural Engineers.
Hantush, M. M., and M. A. Marino. 2001. "Analytical modeling of the influence of denitrifying sediments
on nitrate transport in aquifers with sloping beds." Water Resour. Res.., 37(12), 3177-3192.
Health Management and Biosecurity in U. S. Feedlots. Part III. 1999. USDA APHIS. Veterinary Services.
Centers for Epidemiology and Animal Health. 555 South Howes St. Ft. Collins, CO 80521.
Hitch, Paul H. 1999. "Trends, technology, and challenges for large-scale animal agriculture," in Effects of
Animal Feeding Operations on Water Resources and the Environment. Proceedings of the technical
meetings, Fort Collins, Colorado, aug. 30 - Sep. 1. US Geological Survey Open-File Report 00-24.
Hitt, Kerie J., Barbra C. Ruddy, and Jeffrey D. Stoner. 1999. "Potential exposure of the nation's waters to
animal manure," in Effects of Animal Feeding Operations on Water Resources and Environment.
Proceedings of the technical meetings, Fort Collins, Colorado, Aug. 30 - Sep. 1. US Geological Survey
Open-File Report 00-24.
Hong J.H., Keener Harold M., and Elwell David L. 1998. Preliminary study of the effect of continuous and
intermittent aeration on composting hog manure amended with sawdust. Compost-Science-and-Utilization
6, no. 3:74-88.
Hong J.H., Keener Harold M., and Elwell David L. 1998. The effect of continuous and intermittent aeration
on composting hog manure amended with sawdust - progress report. ASAE Annual International Meeting,
Orlando, Florida, USA, 12-16 July, 1998. 1998, 21 Pp.; ASAE Paper No. 984098.
Hong J.H., Park K. J., and Shon B.K. 1997. Influence of aeration rate on ammonia emission in high rate
composting of dairy manure and rice hulls mixtures. A progress report. In Pap-Am-Soc-Agric-Eng, No.
974114, 8 pp. ASAE Annual International Meeting, St. Joseph, Mich.: AmericanSociety of Agricultural
Hong, J. H., J. Matsuda, and Y. Ikeuchi. 1983. High rapid composting of dairy cattle manure with crops and
forest residues. Trans ASAE 26, no. 2: 533-45.
Hosek, G., D. Leschinsky, S. Irons, and T. J. Safranek. 1997. Multidrug-resistant Salmonella serotypes
Typhimurium-United States, 1996. MMWR Morbid. Mortal, Wkly Rep. 46:308-310.
Hurst, C. J., C. P. Gerba, and I. Cech. 1980. "Effects of environmental variables and soil characteristics on
virus survival in soil." Appl. Environ. Microbio., 40, 1067-1079.
Impellitteri, C.A., Y. Lu, J.K. Saxe, H.E. Allen, and W.J.G. M. Peijnenburg. 2002. Correlation of the
partitioning of dissolved organic matter fractions with the desorption of Cd, Cu, Ni, Pb, and Zn from 18
Dutch soils. Enivon. Intl. 28: 401-410.
Iowa State University. 1995. Land application for effective manure nutrient management. PM-1599, Iowa
State Univ. Extension. Ames, Iowa.
Isbister, J. et al. Ecological Effects of Antibiotics in Runoff from an Eastern Shore Tributary of the
Chesapeake Bay. Wilde, F.D., Britton, L.J., Miller, C.V., and Kolpin, D.W., comps., 2000, Effects of animal
feeding operations on water resources and the environment—proceedings of the technical meeting, Fort
Collins, Colorado, August 30-September 1, 1999: U.S. Geological Survey Open-File Report 00-207, 107p.
Jacobson, L.D., C. Radman, D. Schmidt, and R. Nicalia. 1997b. Odor measurements from manure storage
on Minnesota pig farms. P. 93-100. In: Proc. TLES, Bloomington, MN. May 29-31, 1997. Am. Soc.
Agric. Engin., St. Joseph, MI.
Jacobson, L.D., C.J. Clanton, C. Radman, D. Schmidt, R. Nicalia, and K.A. Janni. 1997a. Comparison of
hydrogen sulfide and odor emissions from animal manure storages. P. 404-412. In: J.A.M. Voermans and
G.J. Monteny (eds). Proc. Int'l. Symp. Animal and Odor Control from Anima Production Facilities,
Vinkeloord, the Netherlands. Oct. 6-10, 1997, Dutch Soc. Agric. Engin., Vinkeloord, the Netherlands.
Jawson, M. D., R. J. Wright, and L. W. Smith. 1998. "U.S. Department of Agriculture's national program
on manure and byproduct utilization." In AFO & GW, 1998, Animal Feeding Operations and Ground
Water: Issues, Impacts, and Solutions - A Conference for the Future., St. Louis, Missouri, 1-4.
Jawson, M.D., L.F. Elliot, K.E. Sexton, and D.H. Fortier. 1982. The effect of cattle grazing on indicator
bacteria in runoff from a Pacific northwest watershed. J. Environ. Qual. 11:621-627.
Jorm, L.R., Lightfoot, N.F., Morgan, K.L.(1990), An epidemiological study of an outbreak of Q fever in a
secondary school, EpidemiolInfect 1990 Jun; 104(3):467-77.
Joshua, R. S., B. J. Macauley, and H. J. Mitchell. 1998. Characterization of temperature and oxygen profiles
in windrow processing systems. Compost-Science-and-Utilization 6, no. 4: 15-28.
Kadlec, R.H. and R.L. Knight. 1996. Treatment Wetlands. CRC Press LLC, Boca Raton, FL.
Kansas State University Agricultural Experiment Station and Cooperative Extension Service. MF2303,
Kanwar, R.S., H. P. Johnson, and J. L. Baker. 1983. "Comparison of simulated and measured nitrate losses
in tile effluent." Trans. Am. Soc. Agric. Eng., 26, 1451-1457.
Kasmanian, R.M., and R.F. Ryank.1996. Agricultural composting in the United States: Trends and driving
forces. Jour. Soil and Water Conservation. May- June: 194-201.
Kellogg, R.L., C.H. Lander, D. Moffitt, and N. Gallehan. 2000. Manure nutrients relative to the capacity of
cropland and pastureland to assimilate nutrients: spatial and temporal trends for the U.S. U.S. Dept. Agric.
Nat. Res. Cons. Serv., Washington D.C.
Kemp, J. S., E. Paterson, S. M. Gammack, M. S. Cresser, andK. Killham. 1992. "Leaching of genetically
modified Pseudomonasfluorescens through organic soils: Influence of temperature, soil pH, and roots."
Bio. Fertil. Soil, 13, 218-224.
Kirchmann, H., and E. Witter. 1989. Ammonia volatilization during aerobic and anaerobic manure
decomposition. Plant and Soil 115: 35-41.
Klinger, Barbara, "Environmental Aspects of Biogas Technology," German Biogas Association.
Knight, R.L., V.W.E. Payne, R.E. Borer, R. A. Clarke, and J.H. Pries. 2000. Constructed Wetlands for
Livestock Wastewater Management. Ecological Engineering, Vol. 15, No. 1-2, pp. 41-55, June 2000.
Kolpin, D., Furlong, E., Meyer, M., Thurman, E., Zaugg, S., Barber, L., and Buxton, H., Pharmaceuticals,
Hormones, and Other Organic Wastewater Contaminants in U.S. Streams, 1999-2000: A National
Reconnaissance. Environmental Science & Technology, vol. 36, No. 6, 2002, pgs!202-1211.
Kolpin, D., Riley, D., Meyer, M., Weyer, P., and Thurman, E., Pharm-Chemical Contamination: A
Reconnaissance for Antibiotics in Iowa Streams, 1999.
Wilde, F.D., Britton,
Korom, S. F., 1992. "Natural denitrification in the saturated zone: A review." Water Re sour. Res., 28, 1657-
Kovacic, David A., Mark B. David, Lowell E. Gentry, Karen M. Starks, and Richard A. Cooke. 2000.
"Effectiveness of constructed wetlands in reducing nitrogen and phosphorous export from agricultural tile
drainage."/. Environ. Qual., 29(4), 1262-1274.
Larney, F., and A. A. Carcamo. 1999. Active vs. passive composting of feedlot cattle manure. In Manure
management '99, June 22-25, 1999, Saskatoon, SK. Proceedings of a tri-provincial conference on manure
management, 400-405. Saskatoon: Saskatchewan Agriculture and Food.
Larney, Francis J. 1999. Composting: Minimizing losses and maximizing nutrients and value. In Best
management practices to protect our soil, water and air. LandWise Inc., Farm Business Management
Program, and AAFRD, 42-45.
Larsen-Royce, E., RJ. Miner, J.C. Buckhouse, and J.A. Moore. 1994. Water-quality benefits of having
cattle manure deposited away from streams. Bioresource Technol. 48:113-118.
Lau, A. K., K. V. Lo, P. H. Liao, and J. C. Yu. 1992. Aeration experiments for swine waste composting.
Bioresour-Technol 41, no. 2: 145-52.
Lau, A. K., P. H. Liao, and K. V. Lo. 1993. Evaluation of swine waste composting in vertical reactors. J-
Environ-Sci-Health,-Part-A:-Environ-Sci-Eng A28, no. 4: 761-77.
Legrand. H. E., V. T. Stringfield. 1973. "Concepts of karst development in relation to interpretation of
surface runoff." U.S. Geol. Surv. Jour. Res., V.I, p. 351-360.
Lemley, Ann. 1987. "U.S.D.A. Research and extension recommendations for groundwater programs." In
Chautauqua Groundwater Workshop for Extension Agents, Chautauqua Institution., Chautauqua, New York,
May 7-9, 1986, Publication #48, Ed. Aletha Rudd, 92-98.
Liao, P. H., A. T. Vizcarra, A. Chen, and K. V. Lo. 1993. Composting of separated solid swine manure. J-
Environ-Sci-Health,-Part-A:-Environ-Sci-Eng. 28 , no. 9: 1889-901.
Lim, Poh-Eng and Mun-Yoon Kiu, 1995. Determination and speciation of heavy metals in sediments of the
Juru River, Penang, Malaysia. Environmental Monitoring and Assessment. 35:85-95.
Liu, B.Y., M.A. Nearing, PJ. Shi, and Z.W. Jia. 2000. Slope length effects on soil loss for steep slopes.
Soil Sci. Soc. Am. J. 64:1759-1763.
Lopez-Real, J. M., and M. Baptista. 1996. A preliminary comparative study of three manure composting
systems and their influence on process parameters and methane emissions. Compost- Science-and-
Utilization 4, no. 3: 71-82.
Lufkin, Christopher, Ted Loudon, Michael Kenny, and James Scott. 1996. Windrow methods compared:
Practical applications of on-farm composting technology. BioCycle 36, no. 12: 76-78.
Lusk, P., "Methane Recovery from Animal Manures: A Current Opportunities Casebook," 3rd Edition,
National Renewable Energy Laboratory, Golden, CO, 1998.
Lusk, P., and Moser, M., "Anaerobic Digestion - Yesterday, Today, and Tomorrow," Ninth European
Bioenergy Conference, Copenhagen, Denmark, UK, June, 1996.
Lusk, Phillip D., "Latest Progress in Anaerobic Digestion," BioCycle, July, 1999, p. 52.
Lusk, Phillip, "Farm-Based Anaerobic Digestion Practices in the U.S.,"
MacKenzie, W.R., Hoxier, NJ. et al 1994. Massive waterborne outbreak of Cryptosporidium infection
associated with a filtered water supply. N. Engl. J Med. 331:161-167.
Magbanua, B.S. and Adams, T.T., "Anaerobic Codigestion of Hog and Poultry Waste," Bioresource
Maguire, R.O., J.T. Sims, and FJ. Coale. 2000. Phosphorus fractionation in biosolids-amended-soils:
relationship to soluble and desorbable phosphorus. Soil Sci. Soc. Am. J. 64: 2018-2024.
Martinez, J. and Peu, P., 2000. Nutrient fluxes from a soil treatment process for pig slurry. Soil Use and
Mathur, S. P., N. K. Patni, and M. P. Levesque. 1990. Static pile passive aeration composting of manure
slurries using peat as a bulking agent. Biological Wastes 34, no. 4: 323-34.
Mawdsley, J. L., R. D. Bardgett, R. J. Merry, B. F. Pain, and M. K. Theodorou. 1995. "Pathogens in
livestock waste, their potential for movement through soil and environmental pollution." Applied Soil
Ecology, 2, 1-15.
Maynard, A. A. 1993. Nitrate Leaching From Compost-Amended Soils.
McCoy, E. L., and C. Hagedorn. 1979. "Quantitatively tracing bacterial transport in saturated soil systems."
Water Air Pollut., 11,467-479.
McBride, M.B. 1994. Trace and toxic elements in soils. In: Environmental Chemistry of Soils. Pp. 308-
341. Oxford Univ. Press, New York, NY.
McDowell, R. W., and A. N. Sharpley. 2001. "Approximating phosphorus release from soils to surface
runoff and subsurface drainage." J. Environ. Qual., 30, 508-520.
McGreer, AJ. 1998. Agricultural Antibiotics and Resistance in Human Pathogens: Villain or Scapegoat?
Can. Med. Assoc. J., Nov 3. 159(9): 1119-1120.
McMurry, S. W., M. S. Coyne, and E. Perfect. 1998. "Fecal coliform transport through intact soil blocks
amended with poultry manure." J. Environ. QuaL, 27, 86-92.
McNeil Technologies, Inc., "Assessment of Biogas-to-Energy Generation Opportunities at Commercial
Swine Operations in Colorado, Department of Energy, Western Regional Biomass Energy Program, Nov.,
Mengis, M., S. L. Schiff, M. Harris, M. C. English, R. Aravena, R. J. Elgood, and A. MacLean. 1999.
"Multiple geochemical and isotopic approaches for assessing groundwater NO3- elimination in riparian
zones." Ground Water, 37(3), 448-457.
Merchant, J.A., M.D., Dr.P.H., Dean, and Ross, R.F., D.V.M., Ph.D. 2002. Iowa Concentrated Animal
Feeding Operations: Air Quality Study: Final Report. Iowa State University and The University of Iowa
Study Group, pp. 1-221.
Midwest Plan Service (MWPS)/Livestock and Poultry Environmental Stewardship Curriculum (LPES).
Lessons 40-44. Web Site: http://www.lpes.org/Lessons/LessonO 1/01_sec5.pdf
Mielke, L. N., and J. R. Ellis. 1976. "Nitrogen in soil cores and ground water under abandoned cattle
feedlots." J. Environ. Qual, 5(1), 71-74.
Millard, Peter S., K.F. Gensheimer, et al. 1994. An Outbreak of Cryptosporidium from Fresh-Pressed Apple
Cider. Journal of the American Medical Association, 212:1592-6.
L.J., Miller, C.V., and Kolpin, D.W., comps., 2000, Effects of animal feeding operations on water resources
and the environment—proceedings of the technical meeting, Fort Collins, Colorado, August 30-September
1, 1999: U.S. Geological Survey Open-File Report 00-207, 107p.
Mohanna, C. and Y. Nys, 1999. Effect of dietary zinc content and sources on the growth, body zinc
deposition and retention, zinc excretion and immune response in chickens. British Poultry Science. 40:108-
Morgan GM, Newman C, Palmer SR, Allen JB, Shepherd W, Rampling AM, Warren RE, Gross RJ,
Scotland SM, Smith FIR. (1998). First recognized community outbreak of haemorrhagic colitis due to
verotoxin-producing Escherichia coli O 157 H7 in the UK. Epidemiology and Infection 101(1):83-91
Morrow, W., P. O'Quinn, J. Barker, G. Erickson, K. Post and M. McGraw. 1995. Composting as a suitable
technique for managing swine mortalities. Swine Health and Production. 56-68.
Moser, Mark A. et. al., "AgSTAR Program: Benefits, Costs and Operating Experience at Seven New
Agricultural Anaerobic Digesters," Oct., 2000. http://www.epa.gov/outreach/agstar/library/ben.html
Moser, Mark A., Mattocks, Richard P., "Benefits, Costs and Operating Experience at Ten Agricultural
Anaerobic Digesters," Proceedings of the Eighth, Des Moines, IA Oct. 9-12, 2000.
Myers, D. N. 1999. "Methods of assessing microbial contamination of surface and ground waters by animal
feeding operations." In Effects of Animal Feeding Operations on Water Resources and the Environment.
Proceedings of the technical meetings, Fort Collins, Colorado, Aug. 30 - Sep. 1. US Geological Survey
Open-File Report 00-24.
Nebraska Department of Environmental Quality. 2001. Environmental Fact Sheet, Air Pollutant
Information. Lincoln, NE. Web Site: www.deq.state.ne.us.
Nelson, Hillary. 1997. The Contamination of Organic Produce by Human Pathogens in Animal Manure.
Ecological Agriculture Projects web site, http://www.eap.mcgill.ca/SFMC-l.htm.
Nicholson, F. A., et al, 1999. Heavy metal contents of livestock feeds and animal manures in England and
Wales. Bioresource Technology. 70:23-31.
North Carolina (State of). Administrative Code 15A NCAC 2H.0200 (Waste Not Discharged to Surface
Waters), Department of Environment, Health and Natural Resources, Division of Water Quality, 1996.
Ohio State University Bulletin, 1998. Tri-State Swine Nutrition Guide. Bulletin 869-98.
Opperman, M. H., L. McBain, and M. Wood. 1987. "Movement of cattle slurry through soil by Eisenia
foetida (Savigny). SoilBiol. Biochem., 19, 741-745.
Overcash, M. R., F. J. Humenik, and J. R. Miner. 1983. "Livestock Waste Management." Vol. I. CRC Press,
Inc., Boca Raton, Florida.
0ygarden, L., J. Kvaerner, and P. D. Jenssen. 1977. "Soil erosion via preferential flow to drainage systems
in clay soils." Geoderma, 76, 65-86.
Parker , D. B., D. D. Schulte, D. E. Eisenhauer. 1999. "Seepage from earthen animal waste ponds and
lagoons - An overview of research results and state regulations." AmericanSociety of Agricultural
Engineers, Transactions oftheASAE, 42(2), 485-493.
Patania, N.L., J.G. Jacangelo, L. Cummings, A. Wilezak, K. Riley, and J. Oppenheimer. 1995.
Optimization of filtration for cyst removal. AWWARF and AWWA Ann. Mtgs. Denver, CO.
Patni, N.K., H.R. Toxopeus, and P.Y. jui. 1985. Bacterial quality of runoff from manured and non-
manured cropland. Trans. Amer. Soc. Agric. Eng. 28: 1871-1877.
Patni, N.K., R. Toxopeus, A.D. Tennant, and F.R. Hore. 1984. Bacterial quality of tile drainage from
manured and fertilized cropland. Water Res. 18: 127-132.
Payne Engineering and CH2M-Hill. 1997. Constructed Wetlands for Animal Waste Treatment: A Manual
on Performance, Design, and Operation With Case Histories. CH2M-Hill, Gainesville, FL, June 1997.
Pell, A. 1997. Manure and microbes: public and animal health problem? J. Dairy Sci. 80:2673-2681.
Penprase, M. Antibiotics found in Shoal Creek, Springfield News-Leader, December 26, 2001.
Pesti, G. M. et al, 1996. Studies on the feeding of cupric sulfate pentahydrate and cupric citrate to broiler
chickens. Poultry Science. 75 (#9): 1086-1091.
Petersen, S. O., A-M Lind, and S. G. Sommer. 1998. Nitrogen and organic matter losses during storage of
cattle and pig manure. Journal of Agricultural Science Cambridge 130, no. 69-79.
Prairie Agricultural Machinery Institute, A Guide to Swine Manure Management Methods, Humboldt,
Saskatchewan, Canada, April 1997. http://www.pami.ca/PDGs/Pami730.pdf
Price, J, 1975. The availability to sheep of copper in pig-slurry and slurry-dressed herbage. Proceedings of
the Nutrition Society. 34 (#1):9A-10A.
Public Health Dispatch: Outbreak of Escherichia coll O157:H7 and Campylobacter Among Attendees of
the Washington County Fair-New York, 1999.
Randall, G. W., J. K. Iragavarapu, and M. A. Scmitt. 2000. "Nutrient Losses in subsurface drainage water
from dairy manure and urea applied to corn." J. Environ. Qual., 29, 1244-1252.
Reed, S.C., R.W. Crites, and I.E. Middlebrooks. 1995. Natural Systems for Waste Management and
Treatment. 2nd edition. McGraw-Hill, Inc., New York, NY.
Reed, St. T., et al, 1993. Copper fractions extracted by Mehlich-3 from soils amended with either CuSO4 or
copper rich pig manure. Commun. Soil Sci. Plant Anal. 24(#9 and 10):827-839.
Reintjes R, Hellenbrand W, Dusterhaus A. (2000) Q-fever outbreak in Dortmund in the summer of 1999.
Results of an epidemiological outbreak study Gesundheitswesen. 2000 Nov;62(l 1):609-14.[Article in
German]Gesundheitsamt der Stadt Dortmund, email@example.com
Report to the State of Iowa Department of Public Health on the Investigation of the Chemical and Microbial
Constituents of Ground and Surface Water Proximal to Large-Scale Swine Operations, 1998.
Richardson, A.J., Frandenberg, R.A., et al. An outbreak of waterborne cryptosporidiosis in Swindon and
Oxfordshire. Epidemiol. Infect. 107:485-495. 1991.
Ritter, W. F., A. E. M. Chirnside. 1990. "Impact of animal waste lagoons on groundwater quality."
Biological Wastes, 34:39-54.
Robens, J. 1998. "Research needs to prevent ground water contamination from animal feeding operations."
In AFO & GW, 1998, Animal Feeding Operations and Ground Water: Issues, Impacts, and Solutions - A
Conference for the Future, St. Louis, Missouri, 105-107
Robertson, John B., and Stephen C. Edberg. 1977. "Natural protection of springs and well drinking water
against surface microbial contamination: I. Hydrogeologic parameters." Critical Reviews in Microbiology,
Rochette, P., E. van Bochove, D. Prevost, D.A. Angers, D. Cote, and N. Bertrand. 2000. soil carbon and
nitrogen dynamics following application of pig slurry for th
and mineral nitrogen. Soil Sci. Soc. Am. J. 64: 1396-1403.
nitrogen dynamics following application of pig slurry for the 19th consecutive year: II. Nitrous oxide fluxes
Rosen, Barry H. 2000. "Waterborne pathogens in agricultural watersheds," NRCS, Watershed Science
Institute, School of Natural Resources, University of Vermont, Burlington.
Rothe, S., et al, 1994. The effect of vitamin C and zinc on the copper-induced increase of cadmium residues
in swine. Zeitschrift Fur Ernahrungswissenschaft. 33(#l):61-67.
Russ, C.F. and Yanko,W.A. 1981. Factors affecting salmonella repopulation in composted sludges. Appl.
Environ. Microbiol. 41:597-602.
Ryden, J. C., J. K. Syers, and R. F. Harris. 1973. "Phosphorus in runoff and streams." Adv. Agron., 25, 1-45.
Rynk, Robert F. 1992. On-farm composting handbook., NRAES-54. Ithaca, NY: Northeast Regional
Agricultural Engineering Service.
Saele, Leland M., "Anaerobic Digester Lagoon with Methane Gas Recovery: First Year Management and
Economics," Conservation Technology Information Center, Purdue University.
http://www.ctic.purdue.edu/core4/nutrient/manuremgmt/Paper31.html, Aug. 7, 2001
Saint-Fort, R., R. M. Raina, and B. Prescott. 1995. "Subsurface quality under a cattle feedlot and adjacent
cropfield." J. Environ. Sci. Health, A 30(3), 637-650.
Sartaj, M., L. Fernandes, andN. K. Patni. 1997. Performance of forced, passive, and natural aeration
methods for composting manure slurries. Trans-ASAE 40, no. 2: 457-63.
Scapegoat? Canadian Medical Association Journal, Nov 3, 1998, 159(9) pp 1119-1120.
Schepers, J. S., and D. D. Francis. 1998. "Manure characterization and nutrient utilization strategies for
crops to minimize environmental risk." In AFO & GW, 1998, Animal Feeding Operations and Ground
Water: Issues, Impacts, and Solutions - A Conference for the Future, St. Louis, Missouri. 96-104.
Sharpe, R.R. and L.A. Harper. 1997. Ammonia and nitrous oxide emissions from sprinkler irrigation
applications of swine effluent. J. Environ. Qual. 26: 1703-1706.
Sharpley, A., W. Gburek, and G. Folmar. 1998. "Integrated Phosphorus and Nitrogen Management in
Animal Feeding Operations for Water Quality Protection." In AFO & GW, 1998, Animal Feeding
Operations and Ground Water: Issues, Impacts, and Solutions - A Conference for the Future, St. Louis,
Shipitalo, MJ. and F. Gibbs. 2000. Potential of earthworm burrows to transmit injected animal wastes to
tile drains. Soil Sci. Soc. Am. J. 64: 2103-2109.
Siddique, M. T., J. S. Robinson, and B. J. Alloway. 2000. "Phosphorus reactions and leaching potential in
soils amended with sewage sludge." J. Environ. Qual., 29(6), 1931-1938.
Simpson, T. W. 1990. Agronomic use of poultry industry waste. Poultry Sci. 70:1126-1131.
Sims, J. T., R. R. Simard, and B. C. Joern. 1998. "Phosphorus loss in agricultural drainage: Historical
perspective and current research." J. Environ. Qual., 27, 277-293.
Smith, M.S., G.W. Thomas, R.E. White, and D. Ritanga. 1985. Transport of Escherichia coli through intact
and disturbed soil columns. J. Environ. Qual. 14: 87-91.
Spencer, J. L., H. Dinel, N. K. Patni, and J. R. Chambers. 1997. Composting strategies to improve
biosecurity and eliminate Salmonella from chicken litter. In: Proceedings seventh annual conference,
exhibits & general meeting, November 5-7, 1997, Montreal, Quebec Composting Council of Canada, 277-
82. Toronto: The Composting Council of Canada.
Spruill, T. B. 1999. "Identification of sources of nitrate in ground water - A feasibility evaluation." In
Effects of Animal Feeding Operations on Water Resources and the Environment. Proceedings of the
technical meetings, Fort Collins, Colorado, Aug. 30 - Sep. 1. US Geological Survey Open-File Report 00-
Steiner, C.G., "Understanding Anaerobic Treatment," Pollution Engineering Online, Feb., 2000.
Stentiford, E.I. 1993.Diversity of Composting Systems, p. 95-110. In H.A.J. Hoitink and H.M. Keener (ed)
Science and Engineering of Composting: Design, Environmental, Microbiological and Utilization Aspects.
Renaissance Publ., Worthington, OH
Stevens, R.S. and RJ. Laughlin. 2001. Cattle slurry affects nitrous oxide and dinitrogen emissions from
fertilizer nitrate. Soil Sci. Soc. Am. J. 65: 1307-1314.
Stoddard, C.S., M.S. Coyne, and J. H. Grove. 1998. Fecal bacterial survival and infiltration through a
shallow agricultural soil: timing and tillage effects. J. Environ. Qual. 27: 1516-1523.
Sweeten, J. M. 1991. "Groundwater Quality Protection for Livestock Operations." Texas Agricultural
Sweeten, J.M. 2001. Animal Production and Air Quality. Agricultural Outlook Forum. Web Site:
http ://www/usda. gov.
Sweeten, J.M., Erickson, L., Woodford, P., Parnell, C.B., Thu, K., Coleman, T., Flocchini, R., Reeder, C.,
Master, J.R., Hambleton, W., Bluhm, G., Tristao, D. 2000. Air Quality Research and Technology Transfer
White Paper and Recommendations for Concentrated Animal Feeding Operations. Washington, DC. Web
Tester, C.F. 1990. Organic amendment effects on physical and chemical properties of a sandy soil. Soil
Science Society of America Journal 54:827-831.
Thu, K.M., Ph.D. 2001. Neighbor Health and Large-Scale Swine Production. In: An Agricultural Safety
and Health Conference: Using Past and Present to May Future Action. National Coalition for Agricultural
Safety and Health. Iowa City, IA. pp. 1-5. Web Site:
Tiquia, S. M. 1999 Composting of spent pig litter in turned and forced-aerated piles. Environmental
Pollution 99, no. 3: 329-37.
Tiquia, S. M., Tarn N.F.Y., and I. J. Hodgkiss. 1997. Effects of bacterial inoculum and moisture adjustment
on composting of pig manure. Environmental Pollution 96, no. 2: 161-71.
Tiquia, S.M, and Tarn N.F.Y. 1998. Salmonella elimination during composting of spent pig litter.
Bioresour-Technol 63, no. 2: 193-96.
Tom-Petersen, A., Hosbond, C., Nybroe, O., 2001. Identification of copper-induced genes in Pseudomonas
fluorescens and use of a reporter strain to monitor bioavailable copper in soil. FEMS Microbiology
United States Department of Agriculture (USD A)/Agriculture Research Service (ARS). ARS National
Programs. Manure and Byproduct Utilization. Action Plan: Component I: Atmospheric Emissions.
Beltsville, MD. Web Site: http://www.nps.ars.usda.gov...rams/programs.htm?npnumber=206&docid=344.
United States Department of Agriculture. 1979. Animal Waste Utilization on Cropland and Pastureland;
Utilization Research Report No. 6. Science and Education Administration, Washington D.C.
United States Department of Agriculture. 1991. Constructed Wetlands for Agricultural Wastewater
Treatment. USD A Natural Resources Conservation Service, Washington, DC.
United States Department of Agriculture. 1995. Handbook of Constructed Wetlands, 5 volumes. USD A
Natural Resources Conservation Service/USEPA Region Ill/Pennsylvania Department of Natural
Resources, Washington, DC.
United States Department of Agriculture. 1996. NRCS. National Engineering Handbook: Agricultural
Waste Management Field Handbook. U.S. Dept. Commerce, NTIS. Springfield, VA.
United States Department of Agriculture. NRCS. 1998. Nutrients available from livestock manure relative
to crop growth requirements. USDA-NRCS. Washington D.C.
United States Environmental Protection Agency, "Aerobic Treatment of Livestock Wastes" 1972.
USDA. 1994. Escherichia coli O157:H7 Issues and ramifications., USDA:APHIS:VS Centers for
Epidemiology and Animal Health, Fort Collins, CO.
USDA. 2000. "Principal Pathogens of Concern. Cryptosporidium and Giardia." Water borne Pathogen
Information Sheet. June.
United States Environmental Protection Agency, 2001. Ammonia Emission Factors from Swine Finishing
Operations. Research Triangle Park, NC. Web Site:
United States Environmental Protection Agency, AgSTAR Program: Guide to Operational Systems., Mar.,
United States Environmental Protection Agency, AgSTAR Program: USDA-NRCS Biogas Interim
Standards, March, 2001. http://www.epa.gov/outreach/agstar/stand_plug.html.
United States Environmental Protection Agency. 1999. North American Treatment Wetland Database v2.0.
R.H. Kadlec, R.L. Knight, S.C. Reed, and R.W. Ruble, eds. Office of Water, Washington, DC. (Available
from Don Brown, USEPA, Cincinnati, OH, 513-569-7630.)
United States Environmental Protection Agency. 2000a. Manual: Constructed Wetlands Treatment of
Municipal Wastewaters. Office of Research and Development, Cincinnati, OH, September 2000. (EPA
United States Environmental Protection Agency. 2000b. Guiding Principles for Constructed Treatment
Wetlands: Providing Water Quality and Wildlife Habitat. Office of Wetlands, Oceans and Watersheds,
Washington, DC, October 2000. (EPA 843-B-00-003.
United States Environmental Protection Agency. 2001. Development Document for the Proposed Revisions
to the National Pollutant Discharge Elimination System Regulation and the Effluent Guidelines for
Concentrated Animal Feeding Operation. Office of Water, Washington, DC, January 2001. (EPA 821-R-
USEPA, 2001, Draft Proceedings of the Workshop on Emerging Infectious Disease Agents and Issues
Associated with Animal Manures, Biosolids and Other Similar By-Products, Vernon-Manor Hotel in
Cincinnati, Ohio; June 4-6, 2001
USEPA. 1998. Environmental Impacts of Animal Feeding Operations, U.S. Environmental Protection
Agency, Office of Water, Standards and Applied Sciences Division, Washington, D.C. 20460, December
USEPA. 2000. "National Management Measures to Control Nonpoint Source Pollution from Agriculture."
Office of Water, Nonpoint Source Control Branch. Draft Report.
USEPA. 2003. Industry Directory for On-Farm Biogas Recovery Systems, Second Edition. Office of Aor
and Radiation, USEPA, Washington, D.C. EPA-430-R-03-001.
University of Georgia College of Agricultural and Environmental Sciences Cooperative Extension Service.
Livestock Newsletter, January-February, 1998.
Valcour, J. E., P. Michel, S. A. McEwen, and J. B. Wilson, Associations between Indicators of Livestock
Farming Intensity and Incidence of Human Shiga Toxin-Producing Escherichia coli Infection, Emerging
Infectious Diseases, Vol. 8, No. 3, March 2002 pp. 252-257
Varel, V.H. 2001. Livestock Manure Odor Abatement with Plant-Derived Oils and Nitrogen Conservation
With Urease Inhibitors. USD A-ARS, U.S. Meat Animal Research Center. Clay Center, NE. Web Site:
Vuorinen, Arja H., and M. H. Saharinen. 1997. Evolution of microbiological and chemical parameters
during manure and straw co-composting in a drum composting system. Agric-Ecosyst-Environ 66, no. 1:
Weidner, R.B., A.G. Christianson, S.R. Weibel, and G.G. Robeck. 1969. Rural runoff as a factor in stream
pollution. J. Water Pollut. Contr. Fed. 41:377-384.
WHO, Health Guidelines for the Use of Wastewater in Agriculture and Aquaculture, Report of a WHO
Scientific Group, World Health Organization, Geneva, WHO Technical Report Series, No. 778, 1989.
Wisconsin Energy Bureau, Department of Administration, "Turning Manure to Energy on Farms, Madison,
Withers, P. J. A., and S. C. Jarvis. 1998. "Mitigating options for diffuse phosphorus loss to water." Soil Use
Manage., 10, 348-354.
Wolf, D.C., J.T. Gilmour, and P.M. Gale. 1988. Estimating potential ground and surface water pollution
from land application of poultry litter. II. Publ. No. 137. Arkansas Water Resources Research Center,
Fayetteville, AR. Web Site: www.epa.gov/ordntrnt/ORD/NRMRL/Pubs/200l/wetlands/625r99010.pdf)
World Animal Sciences, 1987. Animal Production and Environmental Health, B6, Chapter 5, 154-202.
Yale Center for Environmental Law and Policy. Controlling Odor and Gaseous Emission Problems from
Industrial Swine Facilities: A Handbook for All Interested Parties, pp. 1-14 . Web Site:
Young, R.A., T. Huntrods, and W. Anderson. 1980. Effectiveness of vegetated buffer strips in controlling
pollution from feedlot runoff. J. Environ. Qual. 9: 483-487.
Zahn, J.A., DiSpirito, A.A., Do, Y.S., Brooks, B.E., Cooper, E.E., and Hatfield, J.L. 2001. Correlation of
Human Olfactory Responses to Airborne Concentrations of Malodorous Volatile Organic Compounds
Emitted from Swine Effluent. J. Environ. Qual. 30:624-634.
Zahn, J.A., Hatfield, J.L., Do, Y.S., DiSpirito, A.A., Laird, D.A., and Pfeiffer, R.L. 1997. Characterization
of Volatile Organic Emissions and Wastes from a Swine Production Facility. J. Environ. Qual. 26:1687-