Next Article in Journal
Hyperspectral and Chlorophyll Fluorescence Imaging for Early Detection of Plant Diseases, with Special Reference to Fusarium spec. Infections on Wheat
Previous Article in Journal / Special Issue
Effect of Different Feed Structures and Bedding on the Horizontal Spread of Campylobacter jejuni within Broiler Flocks
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:

Microbiological Safety of Chicken Litter or Chicken Litter-Based Organic Fertilizers: A Review

Department of Biological Sciences, Clemson University, SC 29634, USA
Department of Food, Nutrition, and Packaging Sciences, Clemson University, SC 29634, USA
Author to whom correspondence should be addressed.
Agriculture 2014, 4(1), 1-29;
Received: 25 November 2013 / Revised: 10 January 2014 / Accepted: 20 January 2014 / Published: 28 January 2014
(This article belongs to the Special Issue Food Safety Management and Poultry Production)


Chicken litter or chicken litter-based organic fertilizers are usually recycled into the soil to improve the structure and fertility of agricultural land. As an important source of nutrients for crop production, chicken litter may also contain a variety of human pathogens that can threaten humans who consume the contaminated food or water. Composting can inactivate pathogens while creating a soil amendment beneficial for application to arable agricultural land. Some foodborne pathogens may have the potential to survive for long periods of time in raw chicken litter or its composted products after land application, and a small population of pathogenic cells may even regrow to high levels when the conditions are favorable for growth. Thermal processing is a good choice for inactivating pathogens in chicken litter or chicken litter-based organic fertilizers prior to land application. However, some populations may become acclimatized to a hostile environment during build-up or composting and develop heat resistance through cross-protection during subsequent high temperature treatment. Therefore, this paper reviews currently available information on the microbiological safety of chicken litter or chicken litter-based organic fertilizers, and discusses about further research on developing novel and effective disinfection techniques, including physical, chemical, and biological treatments, as an alternative to current methods.

1. Introduction

Chicken litter is a mixture of feces, wasted feeds, bedding materials, and feathers [1,2]. Over 14 million tons of chicken litter is produced every year in the US, most of which is usually recycled and spread on arable land as a low cost organic fertilizer [3,4]. Poultry manure contains significant amounts of nitrogen because of the presence of high levels of protein and amino acids. Owing to its high nutrient content, chicken litter has been considered to be one of the most valuable animal wastes as organic fertilizer [5]. Chicken litter is also the source of human pathogens, such as Salmonella, Campylobacter jejuni, and Listeria monocytogenes, that can potentially contaminate fresh produce or the environment and are frequently associated with foodborne outbreaks [1,6]. Composting of poultry waste prior to the application to agricultural land as an organic fertilizer is usually recommended to control pathogens in the end products. Nonetheless, several studies have demonstrated that some pathogenic cells have the potential to persist in the finished compost and also compost-amended soil [7,8,9]. Another major concern for composting is the possibility of pathogen regrowth [10], indicating that a small population of pathogen that either survives the composting process or gets transferred from the environment may multiply to high populations under favorable conditions.
Currently, physical heat treatment (heat-drying after composting or without composting) is one of the most commonly applied techniques to reduce or eliminate potential pathogens in animal wastes [1,2]. The physically heat-treated chicken litter is recommended and used by produce growers. However, some pathogenic cells may have the potential to become acclimatized to the hostile environment during build-up or composting, cross-protecting them against subsequent high temperature treatment [11,12]. Therefore, some current guidelines for heat-treated animal wastes may not be sufficient to eliminate pathogens from the physically heat-treated chicken litter as organic fertilizer. Land spreading of contaminated chicken litter or chicken litter-based organic fertilizers (fertilizers derived from chicken litter sources) can also potentially lead to the introduction of foodborne pathogens into the food chain. Contamination of fresh produce with fecal pathogenic bacteria in the agricultural environment has been implicated as the main cause of numerous food poisoning outbreaks [13]. Therefore, to ensure the absence of pathogens in the fresh chicken litter, poultry compost, or the physically heat-treated chicken litter, additional approaches such as physical, chemical, and biological treatments, should be considered as another means for pathogen control. Moreover, nutrient retention, fuel cost, efficiency, capital cost, and environmental and regulatory policies will be the principle factors when it comes to making decisions on selected processing techniques [14].
Although the application of poultry litter for commercial farming has rarely been associated with foodborne outbreaks, enhanced consumer awareness of food safety issues has increased the scrutiny of agricultural practices. This review thus focuses on the microbiological safety of chicken litter or chicken litter-based organic fertilizers.

2. Pathogens and Antibiotic-Resistant Bacteria in Chicken Litter or Chicken Litter-Based Organic Fertilizers

Chicken litter contains a large and diverse population of microorganisms. Microbial concentrations in chicken litter can reach up to 1010 CFU/g, and Gram-positive bacteria, such as Actinomycetes, Clostridia/Eubacteria, and Bacilli/Lactobacilli, account for nearly 90% of the microbial diversity [15]. Pathogens in chicken litter represent the major group of bacteria of special interest to litter processors. A variety of pathogens can be found in chicken litter or chicken litter-based organic fertilizers, such as Actinobacillus, Bordetalla, Campylobacter, Clostridium, Corynebacterium, Escherichia coli, Globicatella, Listeria, Mycobacterium, Salmonella, Staphylococcus, and Streptococcus [15,16,17,18,19,20]. While different microbes display different metabolic activities within the litter environment, high levels of background microflora may interfere with the survival and growth of pathogens in chicken litter. Fully understanding the levels and prevalence of human pathogens in chicken litter or chicken litter based-organic fertilizers is essential for developing intervention strategies for controlling produce contamination on farms. As shown in Table 1, microbiological surveys have revealed the prevalence of some foodborne pathogens in chicken litter or chicken litter-based organic fertilizers, depending on pathogen species and serotype, chicken age, season, geographic area, farm handling practice, and so on [19,21,22,23]. For example, Li et al. [23] observed that fecal samples of 18-week-old layer birds had the highest prevalence of Salmonella (55.6%), followed by the 25- to 28-wk birds (41.7%), 75- to 78-wk birds (16.7%) and 66- to 74-wk birds (5.5%). Renwick et al. [22] surveyed randomly selected commercial broiler chicken flocks in Canada to determine flock and management factors associated with the prevalence of Salmonella contamination in the floor litter. They found that the prevalence of Salmonella in floor litter samples was significantly associated with the age of the flock and the region of Canada in which the flock was located.
Active surveillance data on foodborne diseases from the United States reveal that among pathogens associated with foodborne outbreaks, Salmonella, E. coli O157:H7, Campylobacter, and L. monocytogenes are responsible for the majority of outbreaks. Salmonella spp. is the most widely distributed pathogen in chicken litter with poultry and eggs remaining as the predominant reservoir.During 1998–2008, foodborne disease outbreaks caused by Salmonella were associated most commonly with poultry meat products (30%) and eggs (24%) [24]. Chicken eggs can be contaminated with Salmonella either horizontally or vertically. The contamination of egg shell can result from horizontal transmission, such as fecal contact [25]. And vertical transmission of Salmonella has been observed in infected ovaries, oviducts, or infected eggs [26]. Although only low numbers of Salmonella can contaminate eggs via the fecal route, these small populations cannot be ignored. Notably, S. Enteritidis, S. Typhimurium, or S. Heidelberg present in chicken feces may not only penetrate into the interior of eggs but also multiply during storage [27]. Salmonella is more frequently isolated from chicken litter or fecal samples as compared to other pathogens being investigated and its prevalence level can range widely from 0 to 100%. And the population of Salmonella in chicken litter can range from 4 to 1.1 × 105 MPN/g litter [6].
Table 1. Prevalence of foodborne pathogens in chicken litter or chicken litter based-organic fertilizers.
Table 1. Prevalence of foodborne pathogens in chicken litter or chicken litter based-organic fertilizers.
PathogenYear/LocationSample sourceSample typeSample sizePrevalenceReferences
ActinobacillusN.A. a/CanadaBroiler, hen, and turkey Litter samples442%[16]
Campylobacter1995/US19 broiler flocksFecal samples94886%–100%[19]
1996–1997/USPoultryLitter samples intended for dairy cattle feed from 13 dairy ranches104- b[28]
2001/US9 broiler flocksFecal samples45080%–100%[19]
N.A./Australia28 sheds of 28 broiler farmsLitter samples60 sites/shed and three sets of 20 were combined36%[6]
ClostridiumN.A./CanadaPoultryLitter samples4457%[16]
N.A./NigeriaLayerLitter samplesN.A.+c[20]
E. coli1994–1995/USPoultryLitter samples86 (64 composted, 18 not composted, 4 samples not analyzed)- for E. coli O157:H7[29]
1996–1997/USPoultryLitter samples intended for dairy cattle feed from 13 dairy ranches104- for E. coli O157, 8%–15% for non-O157 E. coli[28]
N.A./NigeriaLayerLitter samplesN.A.+[20]
N.A./Australia28 sheds of 28 broiler farmsLitter samples60 sites/shed and three sets of 20 were combined100%[6]
2004–2007/USPoultrySamples of compost heaps with chicken litter or chicken carcassesN.A.26% surface and 6.1% internal samples (1st composting phase); absent in all samples (2nd composting phase)[30]
ListeriaN.A./Australia28 sheds of 28 broiler farmsLitter samples60 sites/shed and three sets of 20 were combined-[6]
2004–2007/USPoultrySamples of compost heaps with chicken litter or chicken carcassesN.A.-[30]
MycobacteriumN.A./CanadaPoultryLitter samples445%[16]
N.A./NigeriaLayersLitter samplesN.A.+[20]
SalmonellaN.A./CanadaPoultryLitter samples447%[16]
N.A./USPoultry from 5 premisesLitter samples19873%–89%[31]
1977/Canada3 broiler flocksLitter samples (top 1.27 to 2.54 cm layer)N.A.0%–2%[32]
1978–1979/Canada60 broiler housesLitter samples15 from each house30%[33]
1980–1981/CanadaBroilerLitter and feces samples36 and 2 for litter and feces samples, respectively19%–89% and 0%–100% for feces and litter, respectively[21]
1989–1990/CanadaBroilerLitter samples1276%[22]
1994–1995/USPoultryLitter samples (64 composted, 18 not composted, and no determination for 4 samples)86-[29]
1996–1997/USPoultryLitter samples intended for dairy cattle feed from 13 dairy ranches104-[28]
Salmonella2002/Nigeria5 poultry farmsFecal samples12038%[34]
2006–2007/HungaryBroilerFecal samples6035%–43%[35]
N.A./USHenFecal samples7817%–56%[23]
N.A./NigeriaLayerLitter samples N.A.+[20]
N.A./US7 broiler farmsFecal samples4206%–39%[36]
N.A./Australia28 sheds of 28 broiler farmsLitter samples60 sites/shed and three sets of 20 were combined71%[6]
2004–2007/USPoultrySamples of compost heaps with chicken litter or chicken carcassesN.A.26% surface and 6.1% internal samples (1st composting phase); absent in all samples (2nd composting phase)[30]
StaphylococcusN.A./CanadaPoultryLitter samples44100%[16]
1994–1995/USPoultryLitter samples (64 composted, 18 not composted, and no determination for 4 samples)86-[29]
N.A./NigeriaLayersLitter samplesN.A.+[20]
StreptococcusN.A./CanadaPoultryLitter samples44100%[16]
a N.A., not applicable; b -, no pathogen or selected microorganism was isolated; c +, pathogen or selected microorganism was isolated.
E. coli is present in chicken litter with the prevalence rate as high as 100%; however, E. coli O157:H7 was not detected in chicken litter samples [28,29] or poultry compost samples [29,30]. The population of E. coli in reused chicken litter can reach up to 9.7 × 104 CFU/g while the population for single use litter has been found to be 4.2 × 105 CFU/g [6]. Campylobacter, followed by Salmonella, is the leading cause of bacterial gastroenteritis due to food consumption [37] and is also likely to be present in poultry wastes. The prevalence of Campylobacter in chicken litter or fecal samples can range from 0 to 100% and its average population level was reported to be ca. 105 CFU/g in fecal samples collected from broiler chicken flocks [19]. L. monocytogenes is usually absent (negative) in chicken litter and poultry compost, and this pathogen therefore appears not to be a significant issue in chicken litter or chicken litter-based organic fertilizers [6,30].
There are also growing concerns about the presence of antibiotic-resistant pathogens in animal manures from both on-farm exposure and off-farm contamination. Widespread dispersal of chicken litter or chicken litter-based organic fertilizers harboring antibiotic-resistant foodborne pathogens can be a serious environmental hazard. Furthermore, horizontal transfer of mobile antibiotic resistance genes from one bacterium to another can possibly occur under some conditions [38]. Nandi et al. [39] reported that Gram-positive bacteria were found to be the major reservoir of Class 1 antibiotic resistance integrons in poultry litter. As antibiotics are routinely used for disease prevention and growth promotion, a low level of antibiotics may select antibiotic-resistance bacteria in the gastrointestinal tract of the animal and also under in vitro conditions when antibiotic-laden manure is applied to the agricultural land [40]. Table 2 lists the presence of antibiotic-resistant bacteria in chicken litter or chicken litter based-organic fertilizers, highlighting the need for better waste management practices by poultry producers.
The prevalence of some antibiotic-resistant bacteria in chicken litter or chicken litter based-organic fertilizers can reach more than 60% for selected microorganisms, while it should be noted that some bacteria, such as E. coli, Enterococcus, and Providencia, are found to be multi-resistant to various antibiotics. It is also known that the increased use of antibiotics in the poultry industry can introduce a selective pressure which leads to the development of resistance or even multi-resistance characteristics in some of the bacterial populations. Moreover, as was observed by Khan et al. [41], erythromycin-resistant Staphylococci, Enterococci, and Streptococci were only isolated from litter samples collected from poultry houses that had used the antibiotics. Isolation of antibiotic-resistant foodborne pathogens from chicken litter or chicken litter based-organic fertilizers raises concerns about possible transmission of these bacteria to fresh produce after land application since these pathogens can potentially transfer to the arable land from contaminated chicken litter or chicken litter-based organic fertilizers, and can also further contaminate surface and ground water through runoff. This suggests the poultry industry should follow prudent management options and safety precautions by establishing more effective disinfection guidelines to reduce the population of antibiotic-resistant pathogens and monitoring the potential infection of subsequent flocks with resistant bacteria. In addition, a judicious and moderate use of antibiotics may also help prevent the emergence of antibiotic resistance in pathogenic bacteria. In the meantime, it is of great significance to identify and characterize various isolated antibiotic-resistant pathogens from chicken litter or chicken litter based-organic fertilizers. Therefore, further research is warranted to evaluate the pathogenicity of these antibiotic-resistant isolates, as well as their persistence in manure-amended soil.
Table 2. Antibiotic-resistant bacteria in chicken litter or chicken litter based-organic fertilizers.
Table 2. Antibiotic-resistant bacteria in chicken litter or chicken litter based-organic fertilizers.
PathogenYear/LocationSample sourceSample typeSample sizeComments bReference
ColiformsN.A. a/US4 turkey farms (8 houses), 10 adult broiler breeder chicken farms (43 houses), and 30 broiler chicken farms (110 houses)Litter samplesN.A.In turkey litter, the percentage of NAL-resistant coliforms ranged from 0.6% to 61.9%. Two farms had houses containing coliforms resistant to ENR and SAR. There was also multiple resistance to AMP, TIO, CAM, KAN on all 4 turkey farms. There were no NAL-resistant isolates from any of the 10 adult broiler breeder chicken farms. All of the 30 broiler chicken farms with NAL-resistant isolates were also resistant to SAR.[42]
E. coli2004–2007/USPoultryChicken litter, carcasses, pine shavings, pine fines, and fresh wood chips30 compost samples of chicken litter and carcasses, 42 compost samples of chicken litter and pine shavings, 18 compost samples of chicken litter with pine fines, and 24 compost samples of chicken litter, carcasses, and fresh wood chipsIsolates from California chicken litter/horse track had higher levels (63%) of resistance to AMP as compared with poultry compost in South Carolina (0%). E. coli isolates from poultry composts on South Carolina farms were found to be more resistant to TET (50%) as compared with isolates in compost from California, which had no resistance to this antibiotic.[43]
N.A./CanadaBroilerLitter samples9All isolates were multiresistant to at least 7 antibiotics.
Resistance to AMO,
TIO, TET, and SA was the most prevalent.
Enterococcus2006/US3 broiler farmsLitter samplesN.A.Resistance levels to CLI and ERY were 68%, 18%, respectively. No isolates were found to be resistant to VAN.[45]
N.A./US60 chicken
Litter samplesN.A.ERY-resistant bacteria were only isolated from litter samples collected from farms that had used the drug.[41]
ProvidenciaN.A./USTurkeyFecal samples11Isolates were found to be resistant to TET, MAC, and SA groups.[46]
Staphylococci2006/US3 broiler farmsLitter samplesN.A.Resistance levels to CLI and ERY were 0% and 57%, respectively.[45]
N.A./USPoultryLitter samples60ERY-resistant bacteria were only isolated from litter samples collected from farms that had used the drug.[41]
StreptococcusN.A./USPoultryLitter samples60ERY-resistant bacteria were only isolated from litter samples collected from farms that had used the drug.[41]
a N.A., not applicable; b NAL: nalidixic acid, ENR: enrofloxacin, SAR: sarafloxacin, AMP: ampicillin, TET: tetracycline, CAM: chloramphenicol, KAN: kanamycin, AMO: amoxicillin, TIO: ceftiofur, SA: sulfonamide, CLI: clindamycin, ERY: erythromycin, VAN: vancomycin, MAC: macrolide.
The gastrointestinal tracts of animals are the natural habitats for most of the enteric pathogens. After being defecated in feces, these pathogens are immediately exposed to a hostile environment with numerous microorganisms to compete for limited nutrients. Botts et al. [47] and Tucker [48] found that S. Pullorum and S. Gallinarum persisted much longer in fresh chicken litter than in built-up litter. Other studies have also shown that some pathogens in fresh chicken manure can initially grow to higher numbers under favorable environmental conditions. Himathongkham and Riemann [49] reported that E. coli O157:H7 and L. monocytogenes were able to multiply by as much as 100-fold for a period of 2 days in fresh chicken manure at 20 °C, whereas S. Typhimurium populations remained stable. Therefore, special attention should be paid to the initial disinfection processing so as to effectively eliminate pathogens from chicken litter.
When animal wastes are introduced into the agricultural field, the antagonistic effect of indigenous soil microorganisms and the hostile condition of soil microcosm are possible factors influencing the length of time that pathogens can persist [50]. According to the Standards for the Growing, Harvesting, Packing, and Holding of Produce for Human Consumption (Proposed Rule) proposed in the U.S. Food and Drug Administration (USFDA) Food Safety Modernization Act (FSMA) [51], growth of human pathogens in biological soil amendments of animal origin could result in the amendment acting as an inoculum that spreads pathogens to covered produce growing area, leading to a likelihood of produce contamination. Previous studies have reported the growth and persistence of human pathogens in chicken manure and manure-amended soil. Islam et al. [52] reported that S. Typhimurium persisted for 203 to 231 days in soils amended with poultry compost, dairy compost, and alkaline-pH-stabilized dairy compost. As pathogens most commonly associated with fresh produce outbreaks, including E. coli, Salmonella, and Listeria, are unlikely to survive at detectable population levels in soil after 270 days [51], it is proposed by FSMA that the waiting period (application interval) between the application of untreated biological soil amendments of animal origin (such as untreated chicken litter) and the harvest of covered produce should be 9 months provided the material is used in a manner that does not contact covered produce during application and minimizes the risk of contamination after application.

3. Food Safety, and Human and Animal Health Issues Associated with Chicken Litter or Chicken Litter-Based Organic Fertilizers

Poultry is one of the commodities most commonly associated with foodborne disease outbreaks in the preceding years. During 2009–2010, the commodities in the 299 outbreaks associated with the most illnesses were eggs (27% of illnesses), beef (11%), and poultry (10%) [53]. Although foodborne disease outbreaks caused by bacterial pathogens reported so far have rarely been linked directly to chicken litter or chicken litter-based organic fertilizers, their risks to contaminate food or environment is considerably high. And there have been some food safety and human health issues associated with chicken litter in recent years.
Feeding poultry litter to dairy and beef cattle is a means of disposing of a waste product while concurrently supplying a low-cost protein feed to cattle [28]. Processed chicken litter has been used as a feed ingredient for almost 40 years in the US [15]. Cattle have the ability to digest low-cost feedstuffs, such as chicken litter, that are not suitable for other livestock species. However, from the hygienic perspective, raw chicken litter may contain some bacterial pathogens, as noted above. Salmonellosis has been reported in cattle that were fed improperly composted broiler litter [54,55]. Chicken litter was also implicated as a possible source of chronic histoplasmosis case in 2003, which was caused by inhaling fungal spores released by Histoplasma capsulatum when the litter was spread on a pasture [56]. Moreover, some of the fungal species that are indigenous to the manure or litter can result in the production of mycotoxins. The specifications suggested by the Association of American Feed Control Officials (AAFCO) require that processed animal waste products as feed ingredient must be free of human pathogenic microorganisms, which could be harmful to animals or could result in residues in human food products or by-products of animals at levels in excess of those allowed by State or Federal statute or regulation [15]. Hence, proper processing to reduce the amount of these microorganisms or render the waste absent of pathogens is required. In addition, feed additives such as antibiotics are also added into poultry diet, which can be excreted as waste by-products used for cattle feed. Although the use of non-therapeutic levels of antibiotics in animal feed is approved and regulated by the USFDA [57], there is still limited information about the specific types and amounts of antibiotics that should be used for this purpose.
Pathogens can be transmitted to humans directly through contact with poultry litter or indirectly through contaminated poultry products. Water may also become contaminated by runoff either from poultry facilities or from excessive land application of poultry waste [58]. Runoff can possibly carry pathogens from the original site of animal manure-applied agricultural fields to water bodies serving as irrigation, drinking, or recreational water sources [59]. Clear understanding of the transport of pathogens potentially present in poultry wastes and its runoff is essential for the establishment of effective control strategies to reduce the adverse impact on environment, food safety, and public health. Sistani et al. [60] compared two methods of poultry litter application, surface broadcast and subsurface banding, to investigate the influence of application methods on E. coli concentration in runoff from tall fescue pasture. E. coli concentration was found to be significantly higher in runoff from broadcast application than subsurface banding treatment. They concluded that subsurface banding of poultry litter into perennial grassland can greatly reduce pathogen losses in runoff as compared to surface-broadcast application. Therefore, the traditional surface-broadcast application of chicken litter onto agricultural land may result in high levels of pathogens on the soil surface that could be potentially transferred to runoff water.
Adequate control of pathogens may require multiple control interventions to achieve significant reduction of pathogens in a poultry waste management system. And there is a need for some good management practices to reduce potential human exposures to these pathogens by effectively controlling them during chicken litter or chicken litter-based organic fertilizer processing.

4. Control of Pathogens in Chicken Litter or Chicken Litter-Based Organic Fertilizers

As previously stated, a variety of pathogenic bacteria may be present in animal wastes including those destined for composting, presenting a risk of human infection when they are utilized for land application. Composting is commonly employed as a pathogen control technique to recycle animal wastes back into the soil to improve its fertility [61]. Heat treatment after composting or without composting is also recommended to reduce or eliminate potential bacterial pathogens in animal wastes. Meanwhile, some physical, chemical, and biological methods have been developed as alternative disinfection techniques for animal waste processing.

4.1. Composting

The interest in composting has greatly increased in recent years because of the need for environmentally acceptable animal waste treatment technologies and also the demand for organic fertilizers in organic agricultural production system. Composting of animal wastes is a spontaneous bio-oxidative process to produce more uniform, concentrated, and safe final products compared to fresh manure, allowing for easy spreading in the soil and also significant elimination of pathogens [62]. Furthermore, initial capital as well as operating and maintenance costs for composting are lower compared with other treatment techniques [63]. Composting can thus be considered as an effective technique which adds value to poultry waste for agricultural applications.

4.1.1. Composting Process

Before land application, chicken litter is usually built-up inside the chicken house during the growing season of broilers. Build-up is a common method of storing solid animal manure or used as bedding materials until it can be composted or applied to cropland as fertilizer. Barker et al. [64] observed that the middle and bottom sections of the built-up broiler litter bed provided a less favorable environment for anaerobes and coliforms than the top section, as the temperature required to reduce or eliminate bacterial loads are not achieved as they are at deeper layers.
Compared to build-up, composting is a controlled process of mixing organic wastes with other ingredients in an appropriate ratio to optimize microbial growth [65]. Composting is typically the biological decomposition process of biodegradable organic wastes in a predominantly aerobic environment by a consortium of microorganisms. Generally, it is a fast biodegradation process, which takes 4–6 weeks of microbial action to break down organic materials to stable and usable organic substances called compost. Composting allows easy handling and elimination of pathogens (including human and plant pathogens), along with the volume reduction of the wastes and the destruction of weed seeds. However, disadvantages of composting are also documented, such as loss of nitrogen and other nutrients during composting, cost of installation and labor, odor, and requirement for available land for storage and operation [62,66]. The cost of transporting chicken litter is a major obstacle facing the more efficient use of this poultry by-product. After composting, the bulk density of chicken litter is increased, which can reduce the cost of transportation [3]. Since composting can result in considerable nitrogen loss, compost producers may need to add amendments, such as straw, peat, woodchip, paperwaste, aluminum sulfate, and zeolite, to the litter to reduce ammonia volatilization during this process [67]. Moreover, although the objective of composting is generally to achieve a stable waste product, it may also affect both the total content and the composition of metals, such as cadmium, copper and zinc, in poultry manure by-products [68].
The process of composting is typically divided into four main phases based on temperature and active microbial community: mesophilic, thermophilic, cooling, and maturation phases [69]. Microbial activity is critical for a satisfactory composting process, in which mesophilic, thermotolerant, and thermophilic bacteria, actinomycetes, and fungi are all extensively involved [70]. Aerobic microbial decomposition generates sufficient heat to increase the temperature of compost mixtures to the thermophilic zone (45 to 75 °C). Temperatures reached in a well-managed compost operation should be within a range of 55 to 65 °C [71]. Such temperatures are well above the thermal death points of mesophilic pathogens, such as E. coli O157:H7 and Salmonella spp. [72]. Besides high temperature, other mechanisms are also known to get involved in the inactivation of foodborne pathogens during composting, including microbial antagonism, production of organic acids, pH change, desiccation and starvation stresses, exposure to ammonia emission, and competition for nutrients [1].
Currently, within the United States, composting of animal wastes is not regulated by any federal agencies. The National Organic Program, administered by the U.S. Department of Agriculture (USDA), includes a composting standard in 7 CFR 205.2 that is aimed to maximize soil fertility and is required to achieve “USDA Certified Organic” status [73]. Similar to USEPA specifications described in 40 CFR Part 503 for regulating land application of Class A composted sewage sludge [74], the FSMA [51] proposed standards for two specific scientifically valid controlled composting processes: (1) Static composting that maintains aerobic conditions at a minimum of 55 °C for three days and is followed by adequate curing, which includes proper insulation; and (2) turned windrow composting to maintain aerobic conditions at a minimum of 55 °C for 15 days with a minimum of five turnings, and is followed by adequate curing, which includes proper insulation. However, a slightly different temperature and time criterion is recommended by the guidelines for composting dead poultry proposed by USDA [65] and adapted from those developed by McCaskey [75], which requires that when the compost has achieved a temperature greater than 50 °C for at least five days, the composting process is adequate to eliminate L. monocytogenes, E. coli O157:H7, and S. Typhimurium.
Composting has been proved to be an effective method to produce organic fertilizers in order to treat the ever-increasing volume of poultry wastes [76,77], which converted the soluble nutrients to more stable organic forms, thus increasing their bioavailability while reducing their susceptibility to loss when applied to agricultural land. Several studies have demonstrated that composting can be an effective way of lowering the level of foodborne pathogens in chicken litter. In some cases, moreover, common foodborne pathogens can be completely eliminated during the composting process. Martinet al. [29] reported that no E. coli O157:H7 and Salmonella spp. was detected in 64 composted poultry litter samples. Brodie et al. [78] also observed the complete elimination of Salmonella, C. jejuni, and L. monocytogenes from poultry compost when temperature exceeded 55 °C. In the work of Macklin et al. [79], chicken litter samples inoculated with Salmonella and C. perfringens were collected after seven days to determine the population of inoculated bacteria that survived. These pathogens were completely eliminated from the composted samples, while it was still recoverable from the samples that were uncomposted. Results from the study of Silva et al. [80] also indicated that the final compost of poultry manure was free of fecal coliforms and Salmonella spp., although a thermophilic phase (temperature > 40 °C) was not verified in the compost pile. Additionally, the findings of Guan et al. [81] demonstrated that composting of chicken manure, when managed to produce sufficiently high temperature, could reduce or degrade heat-sensitive genetically modified Pseudomonas chlororaphis and their transgenes. Therefore, available information on composting of poultry wastes indicates that composting is a suitable and environmentally sound method of reducing or eliminating foodborne pathogens. Furthermore, it should be emphasized that proper composting management is needed to ensure that the process achieves the target level of the time–temperature combination for killing pathogens.

4.1.2. Pathogen Persistence and Regrowth after Composting

The die-off of pathogens during composting may not be extensive or uniform throughout the composting heaps or piles and depends on some environmental factors, such as microbe type, manure physico-chemical characteristics, aeration, and temperature pattern [62]. Therefore, in some cases, a traditional composting technique may not always be sufficient to ensure complete inactivation of pathogens within the entire compost mass. Consequently, persistence of pathogens in poultry compost has been reported. The surface of fresh compost has been identified as the critical location for pathogens to extend the survival or serves as the source of cross-contamination with the rest of the compost mass during heap turning or with the ambient environment. Shepherd et al. [30] detected that 26% and 6.1% of the surface and internal samples from poultry compost heaps were positive for Salmonella during the first phase of composting, respectively. Their results indicated that the conditions at the compost surface are suitable for pathogen survival, and that the complete composting process, including both heating and curing phases, should be confirmed before the compost is considered a finished, pathogen-free product. In another study, compost temperature of 55 °C was unable to inactivate Salmonella, E. coli O157:H7 and L. monocytogenes for more than eight days in poultry compost [82]. Macklin et al. [79] also recovered C. perfringens from five out of six interior chicken litter samples after seven days during in-house composting. Erickson et al. [83] conducted a field study on the fate of three avirulent pathogen surrogates (gfp-labeled E. coli O157:H7 and L. innocua and avirulent S. Typhimurium) in static composting piles of chicken litter and peanut hulls. Salmonella was detected by enrichment in sub-surface samples of static composting piles up to 14 days. Indicator microorganisms were only detected by enrichment in surface samples during the summer after four days of composting, while E. coli O157:H7 and L. innocua were still detectable by direct plating after 28 days in compost piles during the fall and winter trials. All three bacteria could be detected by enrichment in surface samples for 56 days of composting during the winter.
Besides the survival of pathogen during composting, there is also a concern over the possibility of regrowth due to the outside recontamination under open air composting environments and during storage as well. In the study of Kim et al. [10], E. coli O157:H7 increased from ca. 1 to 4.85 log CFU/g in autoclaved dairy compost after seven days, suggesting that a small portion of pathogenic cells that survive the composting process or are cross-contaminated from the environment could multiply to high populations under favorable conditions. In addition, studies have also demonstrated that pathogen growth in compost is influenced by several environmental variables, such as moisture content, temperature, background microflora, and nutrient availability of the composted solids [10,77]. To ensure the microbiological safety of composted chicken litter, environmental factors supporting potential pathogen regrowth after composting need to be identified and monitored. Additionally, outdoor composting is generally exposed to fluctuating environmental conditions, animal intrusion, and reduced efficiency of composting due to climatic conditions, and is not homogeneous in nature and prone to having “cold-spots” that are not properly treated, even with complete turning [84]. It is thus possible that composting can result in a treated chicken litter that may continue to harbor a low level of human pathogens of food safety concern.

4.1.3. Composting Stress and Stress-Induced Cross-Protection

Composting is a very complex and dynamic biological process, which may pose a significant challenge and create many hostile stresses for the survival and growth of human pathogens. Bacterial stress is generally defined as a physical, chemical, or nutritional condition insufficiently severe to kill but leading to sublethal injury of microbes [85]. Some common types of stress associated with the composting process include desiccation, heat shock, and acid stresses [11,12,86].
Desiccation stress. During composting, moisture level in the compost mixture, especially at the surface of compost pile, is reduced rapidly due to evaporation and the self-heating during the thermophilic phase [9]. Water loss through the desiccation process is an important factor affecting the survival and persistence of bacterial pathogens in low-water-activity environmental habitats, such as soil, sand, and compost surface [86].
Heat shock stress. Heat shock occurs when microorganisms are exposed to temperatures above their normal growth range [87]. Temperature during composting process increases gradually, from ambient temperature to the mesophilic range and then to the thermophilic phase, which may consequently cause heat shock or stimulate a concomitant genetic and physiological heat shock response in some population of pathogenic bacteria [86]. Especially during the extended mesophilic phase of composting, some bacterial cells may become acclimatized to sublethal high temperatures before lethal temperatures are reached, allowing them to survive and, in some cases, multiply under stressful conditions. In support of this notion, results of Singh et al. [11] revealed that heat-shocked E. coli O157:H7, Salmonella, and L. monocytogenes at 47.5 °C survived longer in dairy compost than non-heat-shocked cells at composting temperatures of 50, 55 and 60 °C.
Acid stress. Acid stress can occur in low pH conditions when H+ ions cross the bacterial cell membrane and create an acidic intracellular environment. Acid resistance is especially crucial for foodborne pathogens that must survive the hostile acidic condition in the stomach before entering and colonizing the small intestines or colon [88]. Pathogenic cells present in compost of animal origin may become acid-adapted as they are exposed to acidic condition when passing through the gastric tract.
The presence of stressed microorganisms in manure and compost could pose significant public health concerns when applying the contaminated compost to arable land. Stressed cells in chicken litter or chicken litter-based organic fertilizers can initially go undetected during routine microbiological analysis; however, subsequent resuscitation under suitable environments may allow for significant growth and also possible production of toxins and other virulence factors [89]. Many stressed pathogens either retain or exhibit enhanced virulence and invasion, thus making their detection crucial to ensure food safety [90,91]. S. Enteritidis PT4 with enhanced heat and acid resistance has been reported to be more virulent in mice and more invasive in chickens than the non-resistant reference strain [92]. Interestingly, some stresses that are originally part of the host’s defense system are very similar to those occurred in the natural environment [93]. Therefore, it is reasonable to speculate that pathogens may treat stresses encountered during poultry waste composting or build-up as a signal for the expression of virulence factors. When pathogen-contaminated poultry wastes or their composted products are used as organic fertilizer and soil amendment, pathogens with increased virulence could transfer to produce in the field and thus cause serious foodborne disease outbreaks. However, further research is needed to verify this hypothesis.
Bacteria typically respond to stresses by altering their cellular morphology, membrane composition, biological metabolism, and virulence. Such stressed microorganisms produce a series of stress responses that can afford cross-protection against other stresses, indicating that the adaptation to a single sublethal stress may also enhance the tolerance to multiple lethal stresses. In fact, bacteria, especially foodborne pathogens, are frequently exposed to environmental stresses that cross-protect them against various other stresses [85]. Bacterial cells can gradually adapt to the hostile sublethal conditions, causing an adaptive response accompanied by a temporary physiological change that may result in an enhanced stress tolerance [94]. The general stress response identified in most Gram-negative bacteria, such as E. coli, S. Typhimurium, and P. aeruginosa, is regulated by the sigma factor, RpoS (σS) [95]. Induction of RpoS makes bacteria more resistant to environmental stresses, such as high and low temperatures, prolonged starvation, osmotic shock, pH stress, and oxidative stress [96]. Bacteria defective in the gene (rpoS) for RpoS synthesis have proved to be more sensitive to different adverse conditions [97]. Van Hoek et al. [98] reported that a fully functional RpoS system can provide an advantage for survival in the manure-amended soil environment. In their study, E. coli O157 isolates capable of long-term survival in manure-amended soil were all absent of mutations in their rpoS gene; however, the strains not capable of long-term persistence were mutant in their rpoS gene.

4.2. Other Treatments

The common practice of applying poultry wastes to soil as a source of nutrients to crops is of paramount importance in sustainable agriculture. While composting, to some extent, is an effective method for reducing pathogen concentrations in animal manure, pathogens can still survive in the composted products and contribute to soil contamination. Additional appropriate processing and control measures should therefore be adopted to minimize the pathogen contamination of chicken litter. The FSMA also suggests that such biological soil amendments with a residual population of pathogens after composting should require a multiple hurdle approach to minimize the likelihood of introducing pathogens to the field upon which they are applied [51]. There are a variety of physical, chemical, and biological approaches that have the potential to effectively disinfect chicken litter. Several treatment processes have been designed to operate at conditions capable of disinfecting bacterial pathogens in chicken litter, and the extent to which they actually reduce these microorganisms have also been characterized in laboratory and pilot scale field studies.

4.2.1. Physical Treatment Techniques

Physically heat-drying manure or compost to low moisture content after composting or without composting can reduce the volume and weight, which thus lowers transportation costs, though it requires significant energy inputs. Heat-dried products can be much easier to handle and spread uniformly over an agricultural field, especially after they have been further processed into pellets. Table 3 presents the temperature–time requirements and acceptance criteria for the physical heat-drying of soil amendments.
Although a number of organizations or federal agencies offer independent protocol to ensure safe and effective heat treatment for animal manure or biosolids, there were no defined heat sources (dry vs. moist heat), varying time–temperature requirement, and microbial standards among groups. Research on the inactivation effects of thermal processing on pathogens in chicken litter has yielded generally satisfactory results. The main factors influencing pathogen reductions in animal manure by these processes are temperature, duration of treatment, and moisture level [2]. Wilkinson et al. [1] could not detect any S. Typhimurium in fresh poultry litter (30%, 50% and 65% moisture contents) after 1 h wet heat treatment at 55 or 65 °C in water bath. Kim et al. [2] found that a 7-log reduction of Salmonella spp. in fresh chicken litter (30%, 40% and 50% moisture contents) could be achieved by dry heat treatment at 80 °C in a conventional oven for 44.1 to 63.0 min. When they investigated the effect of chicken litter freshness on heat resistance profiles of Salmonella, Salmonella cells in aged chicken litter survived significantly longer than those in fresh chicken litter under any conditions. Ghaly and Alhattab [99] reported that the drying process at 40, 50 and 60 °C reduced the populations of bacteria, yeast and mold, and E. coli in chicken manure by 65.6%–99.8%, 74.1%–99.6% and 99.9%, respectively. Salmonellae were detected in the raw manure and the dried manure samples collected from the 3 cm deep manure layer after drying at 40 °C but not at 50 and 60 °C. Their results indicated that the higher the drying temperature and/or the thinner the manure layer, the more destruction of microorganisms in the dried manure. It should be noted that the aforementioned results on temperature–time combination requirements for eliminating Salmonella varied among studies. However, comparisons between these different studies should be conducted with precaution due to the differences in the composition and moisture level of chicken litter material, Salmonella strain, and also heating source. For example, Messer et al. [100] found that four different kinds of bacterial pathogens in chicken litter were destroyed by dry heat at different temperatures and within different times. Arizona spp., S. Pullorum, S. Typhimurium, and E. coli were destroyed by heat at 47.2 °C for 30 min, 62.8 °C for 30 min, 62.8 °C for 60 min, 68.3 °C for 30 min, respectively. Also, the physiological stage may contribute to the difference in heat resistance of pathogens in chicken litter. The work by Chen et al. [101] demonstrated that Salmonella cells adapted under a desiccation condition survived much longer in aged chicken litter as compared to non-adapted cells when exposed to the same dry heat treatment at 70, 75, 80, 85 and 150 °C. An obvious variability in heat resistance profile among Salmonella serotypes was also observed during thermal exposure, since S. Senftenberg and S. Typhimurium exhibited higher levels of heat resistance than S. Enteritidis and S. Heidelberg.
Table 3. Temperature–time requirements and acceptance criteria for the physical heat-drying of soil amendments.
Table 3. Temperature–time requirements and acceptance criteria for the physical heat-drying of soil amendments.
SourceSoil amendmentTemperature-time requirementAcceptance criterion
Moisture levelMicrobial level
USEPA [74]BiosolidsEither the temperature of the biosolids >80 °C or the wet bulb temperature of the gas in contact with the biosolids as the biosolids leave the dryer >80 °C<10%For Class A biosolids, fecal coliforms: <1000 MPN/g dry weight or Salmonella: <3 MPN/4 g dry weight
National Organic Program [102]Animal manure>65 °C for >60 min<12%Fecal coliforms, Salmonella, and E. coli O157:H7: negative
European Union [103]Animal manure>70 °C for >60 minN.A.E. coli or Enterococaceae: <1000 MPN/g Salmonella: absence in 25 g of sample
California Leafy Green Products Handler Marketing Agreement [104]Animal manureEither the process has been validated by a recognized authority or is subject to 150 °C for 60 min<30%Fecal coliforms, Salmonella, and E. coli O157:H7: negative or less than detection limit
a N.A., not applicable.
According to the FSMA [51], chicken manure may be physically heat-treated to create a dried, pelleted material that is functionally sterile due to the high heat used during production; however, it has been observed that if the heat treatment is not uniform, the end product may still harbor human pathogens and pose a likelihood of the material being recolonized by these pathogens, leading to the possible contamination of any covered produce to which it is applied. Moreover, physically heat-treated poultry manure pellets would be expected to have limited microorganism content including competitive native microflora of foodborne pathogens, which may provide an opportunity for the potential growth of foodborne pathogens in the event of pellet contamination. The significant energy costs for heat-drying manure or compost at high temperature are also in great contrast to the self-heating generated by microbial respiration during the composting process. The physical heat-drying of manure or compost may largely increase the volatilization of ammonia–nitrogen and reduce the total nitrogen level in the finished products. Additionally, manure or compost that is physically heat-dried at a high temperature instead of going through a curing phase at an ambient temperature is not considered to be as microbiologically active as the composted products.
Besides traditional thermal processing, some other non-thermal physical methods have also been studied to control foodborne pathogens in chicken litter. Barbour et al. [105] evaluated the impact of soil solarization on reduction of indicator microorganisms of fecal contamination in chicken manure-treated soils. The percentage reductions in counts in chicken manure-treated soil collected at 20 cm depth after solarization were: 26.3% (S. aureus), 45.5% (total bacteria), 71.3% (fungi), 81.8% (C. perfringes), 92.6% (fecal coliforms) and 100.0% (non-lactose fermenting bacteria). Significantly, UV disinfection may be an effective treatment for reducing pathogen concentrations in animal wastes, while retaining the nutrient content for crop production. Oni et al. [106] investigated the effect of UV radiation on the survival of Salmonella when present on dried turkey manure particles. They observed that Salmonella exposed to UV in a thin layer of cells in saline that were directly placed in a petri dish showed a 5-log decline within 80 min, as compared to the 1.5-log decrease in turkey manure dispersed as a thin layer on a petri dish, suggesting the presence of manure particles significantly (p < 0.05) protected Salmonella from UV exposure.

4.2.2. Chemical Treatment Techniques

Alum treatment has been widely used to reduce pathogens before land application of chicken litter [107], and it can also be applied as an effective way to reduce ammonia volatilization and water-soluble phosphorus runoff from poultry litter in chicken houses [108]. Pathogens in poultry wastes, such as Salmonella and Campylobacter, have been shown to be reduced significantly or eliminated by alum treatment [109,110,111]. Rothrock et al. [107] used denatured gradient gel electrophoresis (DGGE) and quantitative real-time polymerase chain reaction (PCR) to characterize pathogenic microbial communities in alum-treated poultry litter. Alum addition (10% wt/wt) resulted in significant reductions in C. jejuni, E. coli, and Clostridium/Eubacterium populations by the end of the first month. The concentrations of Salmonella spp. were below detection limit (<5 × 103 cell/g litter) throughout the entire experiment. Similarly, when Gandhapudi et al. [108] studied the immediate effects of alum on potential nitrification in poultry manure, slurries with alum-treated poultry manure reduced the population of fecal bacteria, presumably because of the pH stress that suppressed bacterial growth. However, labor requirements to apply alum to chicken litter and mix them sufficiently may be a limiting factor.
Lime in the form of quicklime (CaO) or hydrated lime [Ca(OH)2] has also been reported to effectively disinfect and stabilize chicken litter by raising the pH of the waste to 12 or increasing the temperature by exothermic reaction, which are beyond the tolerance ranges of most enteric pathogens [112,113]. The disinfection efficacy of quicklime is also attributed to the dehydration in the poultry litter. With reduced water availability, bacteria will need more energy to absorb water from the litter for metabolic processes, making survival more difficult or even impossible [114]. However, there may be some additional costs to consider such as human labor to mix and haul the lime. Maguire et al. [115] applied 10% quicklime to 20% solid broiler litter and reduced the total plate counts from 793,000 to 6500 CFU/mL, which, as they indicated, could reflect the fate of many organisms, such as Salmonella. Bennett et al. [116] found that the addition of lime (5%, 10% and 20%) to poultry litter significantly reduced the recovery incidence of S. Enteritidis within 24 h. Nevertheless, Bennett et al. [117] verified that the effects of 0%, 1%, 2% and 5% of lime addition on turkey litter did not lead to a reduction in Campylobacter or Salmonella, which are contradictory to the above findings, but lime treatment did reduce the population of aerobic bacteria. This difference may be explained by differences in the composition of poultry litter sample and also the lime concentration applied.
Ammonia can also cause a significant reduction of non-spore-forming pathogens in a stacked manure pile [118,119]. There is, however, a lack of comprehensive research concerning this area. The limited information available on the effect of ammonia gas on common pathogens in chicken litter shows that generally it results in a significant reduction of pathogens. Himathongkham and Riemann [49] evaluated the effect of drying and/or exposure to ammonia on S. Typhimurium, E. coli O157:H7 and L. monocytogenes in chicken manure. Drying to a moisture content of 10% followed by gassing with ammonia for 72 h as in an amount of 1% of the manure wet weight resulted in an 8-log reduction of S. Typhimurium and E. coli O157:H7, and 4-log reduction for L. monocytogenes. However, some environmental issues associated with potential pollution impacts of applying ammonia to chicken litter include ammonia emissions as aerial contaminants [120].
Fontenot et al. [121] investigated the effects of various processing techniques on sterilizing broiler litter. Heating at 150 °C for 1 or 2 h, dry heating at 100 °C for 48 h, autoclaving, beta-propiolactone treatment, or ethylene oxide fumigation was ineffective in completely sterilizing the litter. The only effective method was dry heat at 150 °C for a minimum of 3 h. Extensive studies were conducted by Caswell et al. [122] investigating the effectiveness of paraformaldehyde addition and ethylene oxide fumigation on pasteurization of broiler litter. They found that ethylene oxide treatment and dry heat at 150 °C following the addition of paraformaldehyde were all effective in reducing coliforms and total bacteria in broiler litter from >30,000 CFU/g to <2000 CFU/g. Seltzer et al. [123] found that the addition of 1, 3, or 7 g of paraformaldehyde per 100 g of fresh chicken feces reduced total bacteria counts from 2.2 × 109 CFU/g for untreated feces to 1.6 × 108, 1000 and 0 CFU/g, respectively.
Chlorine is an effective disinfection method commonly used for drinking water; however, the high organic matter found in chicken litter may largely diminish the effectiveness of chlorine. Murray et al. [124] concluded that chlorination, while initially reducing the total population of bacteria in sewage, may greatly increase the proportions of antibiotic-resistant pathogenic bacteria. It is still uncertain whether chlorination specifically induces modifications and changes in antibiotic resistance in some bacterial populations. Additionally, Munir et al. [125] reported that chlorination did not contribute to a significant reduction of antibiotic resistant genes and antibiotic resistant bacteria. The efficacy of chlorination can be substantially impacted by the presence of suspended organic matter, which may significantly lower the effective chlorine concentration which bacterial pathogens can be exposed to, and therefore require a higher amount of chlorine [14]. Without extensive pre-treatment, it is possible that manure-derived waste will have substantial interfering substances that will make chlorination less effective. Furthermore, the chemical reactions between chlorine and organic matter, nitrogen-containing compounds, or ammonia in chicken litter or chicken litter-based organic fertilizers when they are exposed to each other may also generate carcinogenic by-products, posing great risk to human health when applying them to agricultural land [126].
While effective in reducing pathogen levels, most of the current chemical treatment techniques are not economically feasible for large-scale chicken litter processing. Meanwhile, the interferences of high loads of endogenous non-pathogenic microorganisms in chicken litter may also influence the efficacy of chemical treatments on the killing of target pathogens.

4.2.3. Biological Control Techniques

To ensure that pathogens are eliminated from chicken litter or chicken litter-based organic fertilizers before application to agricultural land, some innovative biological control approaches have also been explored. The results obtained in the study of Erickson et al. [127] revealed the significant inactivation effect of soldier fly larvae (Hermetia illucens L.) against foodborne pathogens in chicken manure. After two days, Salmonella population in chicken manure containing larvae had decreased by 4-log CFU/g. A 6-log reduction in the population of E. coli O157:H7 in chicken manure was also observed after adding larvae for three days. Yongabi et al. [128] designed a simple plastic anaerobic digester to disinfect contaminated poultry feces while providing biogas and pathogen-free fertilizer. Following anaerobic digestion of poultry feces for 37 days, both coliform and E. coli counts decreased drastically. It was also reported by Krylova et al. [129] that high levels of ammonium (>30 g/L) during anaerobic digestion of poultry litter resulted in a decrease in the numbers of all physiological microbial groups. A study on bacteriophage has also demonstrated its effectiveness for biological control of pathogens in compost. Heringa et al. [130] applied a five-strain bacteriophage mixture to dairy manure compost inoculated with S. Typhimurium. They found that bacteriophage treatment resulted in a greater than 2-log-unit reduction within 4 h. And since bacteriophages are host-specific, unlike physical or chemical treatments, it will not significantly alter the background microbial community in animal wastes. Therefore, application of bacteriophage to chicken litter or chicken litter-based organic fertilizers may be another promising biological control technique during the preharvest stage.

5. Conclusions

Raw chicken litter has been widely applied to arable land as organic fertilizer or soil amendment to improve the soil fertility and structure. To prevent possible microbiological safety issues for the environment and food crops grown in the field, practical and effective treatments should be developed specifically for raw chicken litter prior to land application. Composting, commonly used on farms, can inactivate large populations of human pathogens; however, studies have revealed that some pathogens can survive the composting process due to improper composting or cross-contamination. As a result, a small population of pathogenic cells may survive or regrow in the finished compost products under favorable conditions. Physical, chemical, and biological treatments can be alternative ways for pathogen inactivation but may not always lead to the complete elimination of foodborne pathogens in chicken litter or chicken litter-based organic fertilizers. Furthermore, some cells may become stress-adapted during build-up or composting, which cross-protect them against these subsequent treatments. Based on the hurdle concept, each kind of treatment can be used in combination with other disinfection strategies to potentiate microbial lethality. In order to effectively inactivate pathogens in chicken litter, it would be plausible to design a multi-step treatment with composting as the first step to kill large populations of pathogens, and then apply additional treatments to further eliminate the remaining cells. These systems with multiple treatments involved can be efficient in eliminating pathogens in chicken litter when proper control measures are in place and adopted.
Although chicken litter is considered a potential source of foodborne pathogens, this does not suggest that every portion of the litter contains all the various kinds of pathogens that have been reported or that they will be present at maximally reported prevalence. Nonetheless, treatment techniques should still be developed to inactivate the most resistant and persistent types of pathogens possibly to be encountered. Most of the studies on physical, chemical, and biological treatment techniques have attempted to quantify reductions of different bacterial pathogens or indigenous microorganisms in chicken litter or its composted products. Some estimates of pathogen reductions are uncertain and based only on limited lab studies with few pathogens, including indicator microbes (primarily fecal coliforms). However, it is still not clear whether the fate of such fecal indicator bacteria properly represents the responses of various human pathogens. Moreover, not all fecal coliforms or tested pathogens arise from animal feces, and they have some non-fecal environmental sources, which makes it more difficult to investigate the fate of pathogens in animal wastes during different treatments. Therefore, future studies should focus on evaluating pathogen survival for different treatments using a wide range of conditions commonly encountered during build-up or composting.


This work was partially supported by a grant from the Center for Produce Safety, University of California, Davis.

Conflicts of Interest

The authors declare no conflict of interest.


  1. Wilkinson, K.G.; Tee, E.; Tomkins, R.B.; Hepworth, G.; Premier, R. Effect of heating and aging of poultry litter on the persistence of enteric bacteria. Poult. Sci. 2011, 90, 10–18. [Google Scholar] [CrossRef]
  2. Kim, J.; Diao, J.; Shepherd, M.W., Jr.; Singh, R.; Heringa, S.D.; Gong, C.; Jiang, X. Validating thermal inactivation of Salmonella spp. in fresh and aged chicken litter. Appl. Environ. Microbiol. 2012, 78, 1302–1307. [Google Scholar] [CrossRef]
  3. Moore, P.A., Jr.; Daniel, T.C.; Sharpley, A.N.; Wood, C.W. Poultry manure management: Environmentally sound options. J. Soil Water Conserv. 1995, 50, 321–327. [Google Scholar]
  4. Enticknap, J.J.; Nonogaki, H.; Place, A.R.; Hill, R.T. Microbial diversity associated with odor modification for production of fertilizers from chicken litter. Appl. Environ. Microbiol. 2006, 72, 4105–4114. [Google Scholar] [CrossRef]
  5. Wilkinson, S.R. Plant nutrient and economic value of animal manures. J. Anim. Sci. 1979, 48, 121–133. [Google Scholar]
  6. Chinivasagam, H.N.; Redding, M.; Runge, G.; Blackall, P.J. Presence and incidence of foodborne pathogens in Australian chicken litter. Br. Poult. Sci. 2010, 51, 311–318. [Google Scholar]
  7. Lemunier, M.; Francou, C.; Rousseaux, S.; Houot, S.; Dantigny, P.; Piveteau, P.; Guzzo, J. Long-Term survival of pathogenic and sanitation indicator bacteria in experimental biowaste composts. Appl. Environ. Microbiol. 2005, 71, 5779–5786. [Google Scholar]
  8. You, Y.; Rankin, S.C.; Aceto, H.W.; Benson, C.E.; Toth, J.D.; Dou, Z. Survival of Salmonella enterica serovar Newport in manure and manure-amended soils. Appl. Environ. Microbiol. 2006, 72, 5777–5783. [Google Scholar]
  9. Shepherd, M.W.; Liang, P.; Jiang, X.; Doyle, M.P.; Erickson, M.C. Fate of Escherichia coli O157:H7 during on-farm dairy manure-based composting. J. Food Protect. 2007, 70, 2708–2716. [Google Scholar]
  10. Kim, J.; Luo, F.; Jiang, X. Factors impacting the regrowth of Escherichia coli O157:H7 in dairy manure compost. J. Food Protect. 2009, 72, 1576–1584. [Google Scholar]
  11. Singh, R.; Jiang, X.; Luo, F. Thermal inactivation of heat-shocked Escherichia coli O157:H7, Salmonella, and Listeria monocytogenes in dairy compost. J. Food Protect. 2010, 73, 1633–1640. [Google Scholar]
  12. Singh, R.; Jiang, X. Thermal inactivation of acid-adapted Escherichia coli O157:H7 in dairy compost. Foodborne Pathog. Dis. 2012, 9, 741–748. [Google Scholar] [CrossRef]
  13. Doyle, M.P.; Erickson, M.C. Summer meeting 2007—The problems with fresh produce: An overview. J. Appl. Microbiol. 2008, 105, 317–330. [Google Scholar] [CrossRef]
  14. Kelleher, B.P.; Leahy, J.J.; Henihan, A.M.; O’Dwyer, T.F.; Sutton, D.; Leahy, M.J. Advances in poultry litter disposal technology–A review. Bioresource Technol. 2002, 83, 27–36. [Google Scholar] [CrossRef]
  15. Bolan, N.S.; Szogi, A.A.; Chuasavathi, T.; Seshadri, B.; Rothrock, M.J., Jr.; Panneerselvam, P. Uses and management of poultry litter. World’s Poult. Sci. J. 2010, 66, 673–698. [Google Scholar] [CrossRef]
  16. Alexander, D.C.; Carrière, J.A.; McKay, K.A. Bacteriological studies of poultry litter fed to livestock. Can. Vet. J. 1968, 9, 127–131. [Google Scholar]
  17. Lovett, J.; Messer, J.W.; Read, R.B. The microflora of Southern Ohio poultry litter. Poult. Sci. 1971, 50, 746–751. [Google Scholar] [CrossRef]
  18. Lu, J.; Sanchez, S.; Hofacre, C.; Maurer, J.J.; Harmon, B.G.; Lee, M.G. Evaluation of broiler litter with reference to the microbial composition as assessed by using 16S rRNA and functional gene markers. Appl. Environ. Microbiol. 2003, 69, 901–908. [Google Scholar] [CrossRef]
  19. Stern, N.J.; Robach, M.C. Enumeration of Campylobacter spp. in broiler feces and in corresponding processes carcasses. J. Food Protect. 2003, 66, 1557–1563. [Google Scholar]
  20. Ngodigha, E.M.; Owen, O.J. Evaluation of the bacteriological characteristics of poultry litter as feedstuff for cattle. Sci. Res. Essays 2009, 4, 188–190. [Google Scholar]
  21. Higgins, R.; Malo, R.; René-Roberge, E.; Gauthier, R. Studies on the dissemination of Salmonella in nine broiler-chicken flocks. Avian Dis. 1982, 26, 26–33. [Google Scholar] [CrossRef]
  22. Renwick, S.A.; Irwin, R.J.; Clarke, R.C.; McNab, W.B.; Poppe, C.; McEwen, S.A. Epidemiological associations between characteristics of registered broiler chicken flocks in Canada and the Salmonella culture status of floor litter and drinking water. Can. Vet. J. 1992, 33, 449–458. [Google Scholar]
  23. Li, X.; Payne, J.B.; Santos, F.B.; Levine, J.F.; Anderson, K.E.; Sheldon, B.W. Salmonella populations and prevalence in layer feces from commercial high-rise houses and characterization of the Salmonella isolates by serotyping, antibiotic resistance analysis, and pulsed field gel electrophoresis. Poult. Sci. 2007, 86, 591–597. [Google Scholar]
  24. Centers for Disease Control and Prevention (CDC). Surveillance for foodborne disease outbreaks—United States, 1998–2008. In Morbid. Mortal. Weekly Rep. (MMWR); 2013; 62, pp. 1–34. [Google Scholar]
  25. Forsythe, R.H.; Ross, W.J.; Ayres, J.C. Salmonella recovery following gastro-intestinal and ovarian inoculation in the domestic fowl. Poult. Sci. 1967, 46, 849–855. [Google Scholar] [CrossRef]
  26. Foley, S.L.; Nayak, R.; Hanning, I.B.; Johnson, T.J.; Han, J.; Ricke, S.C. Population dynamics of Salmonella enterica serotypes in commercial egg and poultry production. Appl. Environ. Microbiol. 2011, 77, 4273–4279. [Google Scholar] [CrossRef]
  27. Schoeni, J.L.; Glass, K.A.; McDermott, J.L.; Wong, A.C.L. Growth and penetration of Salmonella enteritidis, Salmonella heidelberg and Salmonella typhimurium in eggs. Int. J. Food Microbiol. 1995, 24, 385–396. [Google Scholar] [CrossRef]
  28. Jeffrey, J.S.; Kirk, J.H.; Atwill, E.R.; Cullor, J.S. Research notes: Prevalence of selected microbial pathogens in processed poultry waste used as dairy cattle feed. Poult. Sci. 1998, 77, 808–811. [Google Scholar]
  29. Martin, S.A.; McCann, M.A.; Waltman, W.D. Microbiological survey of Georgia poultry litter. J. Appl. Poult. Res. 1998, 7, 90–98. [Google Scholar]
  30. Shepherd, M.W.; Liang, P.; Jiang, X.; Doyle, M.P.; Erickson, M.C. Microbiological analysis of composts produced on South Carolina poultry farms. J. Appl. Microbiol. 2010, 108, 2067–2076. [Google Scholar]
  31. Smyser, C.F.; Snoeyenbos, G.H. Evaluation of several methods of isolating salmonellae from poultry litter and animal feedstuffs. Avian Dis. 1969, 13, 134–141. [Google Scholar] [CrossRef]
  32. Bhargava, K.K.; O’Neil, J.B.; Prior, M.G.; Dunkelgod, K.E. Incidence of Salmonella contamination in broiler chickens in Saskatchewan. Can. J. Comp. Med. 1983, 47, 27–32. [Google Scholar]
  33. Long, J.R.; DeWitt, W.F.; Ruet, J.L. Studies on Salmonella from floor litter of 60 broiler chicken houses in Nova Scotia. Can. Vet. J. 1980, 21, 91–94. [Google Scholar]
  34. Orji, M.U.; Onuigbo, H.C.; Mbata, T.I. Isolation of Salmonella from poultry droppings and other environmental sources in Awka, Nigeria. Int. J. Infect. Dis. 2005, 9, 86–89. [Google Scholar]
  35. Nógrády, N.; Kardos, G.; Bistyák, A.; Turcsányi, I.; Mészáros, J.; Galántai, Z.; Juhász, A.; Samu, P.; Kaszanyitzky, J.E.; Pászti, J.; et al. Prevalence and characterization of Salmonella infantis isolates originating from different points of the broiler chicken-human food chain in Hungary. Int. J. Food Microbiol. 2008, 127, 162–167. [Google Scholar] [CrossRef]
  36. Alali, W.Q.; Thakur, S.; Berghaus, R.D.; Martin, M.P.; Gebreyes, W.A. Prevalence and distribution of Salmonella in organic and conventional broiler poultry farms. Foodborne Pathog. Dis. 2010, 7, 1363–1371. [Google Scholar] [CrossRef]
  37. Sidh, J.P.S.; Toze, S.G. Human pathogens and their indicators in biosolids: A literature review. Environ. Int. 2009, 35, 187–201. [Google Scholar] [CrossRef]
  38. Rensing, C.; Newby, D.T.; Pepper, I.L. The role of selective pressure and selfish DNA in horizontal gene transfer and soil microbial community adaptation. Soil Biol. Biochem. 2002, 34, 285–296. [Google Scholar] [CrossRef]
  39. Nandi, S.; Maurer, J.J.; Hofacre, C.; Summers, A.O. Gram-positive bacteria are a major reservoir of Class 1 antibiotic resistance integrons in poultry litter. Proc. Natl. Acad. Sci. USA 2004, 101, 7118–7122. [Google Scholar] [CrossRef]
  40. Levy, S.B. The Antibiotic Paradox: How Miracle Drugs are Destroying the Miracle; Plenum Publishing: New York, NY, USA, 1992. [Google Scholar]
  41. Khan, A.A.; Nawaz, M.S.; Khan, S.A.; Steele, R. Detection and characterization of erythromycin-resistant methylase genes in Gram-positive bacteria isolated from poultry litter. Appl. Microbiol. Biotechnol. 2002, 59, 377–381. [Google Scholar] [CrossRef]
  42. Hofacre, C.L.; Cotret, A.R.; Maurer, J.J.; Garritty, A.; Thayer, S.G. Presence of fluoroquinolone-resistant coliforms in poultry litter. Avian Dis. 2000, 44, 963–967. [Google Scholar]
  43. Heringa, S.; Kim, J.; Shepherd, M.W.; Singh, R.; Jiang, X. The presence of antibiotic resistance and integrons in Escherichia coli isolated from compost. Foodborne Pathog. Dis. 2010, 7, 1297–1304. [Google Scholar] [CrossRef]
  44. Furtula, V.; Farrell, E.G.; Diarrassouba, F.; Rempel, H.; Pritchard, J.; Diarra, M.S. Veterinary pharmaceuticals and antibiotic resistance of Escherichia coli isolates in poultry litter from commercial farms and controlled feeding trials. Poult. Sci. 2010, 89, 180–188. [Google Scholar]
  45. Grahama, J.P.; Evans, S.L.; Price, L.B.; Silbergeld, E.K. Fate of antimicrobial-resistant enterococci and staphylococci and resistance determinants in stored poultry litter. Environ. Res. 2009, 109, 682–689. [Google Scholar] [CrossRef]
  46. Chander, Y.; Goyal, S.M.; Gupta, S.C. Antimicrobial resistance of Providencia spp. isolated from animal manure. Vet. J. 2006, 172, 188–191. [Google Scholar] [CrossRef]
  47. Botts, C.W.; Ferguson, L.C.; Birkeland, J.M.; Winter, A.R. The influence of litter on the control of salmonella infections in chicks. Am. J. Vet. Res. 1952, 13, 562–565. [Google Scholar]
  48. Tucker, J.F. Survival of salmonellae in built-up litter for housing of rearing and laying fowls. Br. Vet. J. 1967, 123, 92–103. [Google Scholar]
  49. Himathongkham, S.; Riemann, H. Destruction of Salmonella typhimurium, Escherichia coli O157:H7 and Listeria monocytogenes in chicken manure by drying and/or gassing with ammonia. FEMS Microbiol. Lett. 1999, 171, 179–182. [Google Scholar] [CrossRef]
  50. Fenlon, D.R.; Ogden, I.D.; Vinten, A.; Svoboda, I. The fate of Escherichia coli and E. coli O157 in cattle slurry after application to land. J. Appl. Microbiol. 2000, 88, 149S–156S. [Google Scholar] [CrossRef]
  51. U. S. Food and Drug Administration (USFDA). Standards for the Growing, Harvesting, Packing, and Holding of Produce for Human Consumption (Proposed Rule). In FDA Food Safety Modernization Act (FSMA); U. S. Food and Drug Administration (USFDA): Silver Spring, MD, USA, 2013. [Google Scholar]
  52. Islam, M.; Morgan, J.; Doyle, M.P.; Phatak, S.C.; Millner, P.; Jiang, X.P. Fate of Salmonella enterica serovar Typhimurium on carrots and radishes grown in fields treated with contaminated manure composts or irrigation water. Appl. Environ. Microbiol. 2004, 70, 2497–2502. [Google Scholar] [CrossRef]
  53. Centers for Disease Control and Prevention (CDC). Surveillance for foodborne disease outbreaks-United States, 2009–2010. In Morbid. Mortal. Weekly Rep. (MMWR); 2013; 62, pp. 41–47. [Google Scholar]
  54. Pugh, D.G.; Rankins, D.L.; Powe, T.; D’Andrea, G. Feeding broiler litter to beef cattle. Vet. Med. 1994, 89, 661–664. [Google Scholar]
  55. Pugh, D.G.; Wenzel, J.G.W.; D’Andrea, G. A survey on the incidence of disease in cattle fed broiler litter. Vet. Med. 1994, 89, 665–667. [Google Scholar]
  56. Man Claims Poultry Litter Caused Illness, Food Safety News. Available online: (accessed on 8 January 2014).
  57. U. S. Food and Drug Administration (USFDA). FDA ApprovedAnimal Drug Products (Green Book); U. S. Food and Drug Administration (USFDA): Silver Spring, MD, USA, 2004.
  58. Berry, E.D.; Woodbury, B.L.; Nienaber, J.A.; Eigenberg, R.A.; Thurston, J.A.; Wells, J.E. Incidence and persistence of zoonotic bacterial and protozoan pathogens in a beef cattle feedlot runoff control-vegetative treatment system. J. Environ. Qual. 2007, 36, 1873–1882. [Google Scholar] [CrossRef]
  59. Thurston-Enriquez, J.A.; Gilley, J.E.; Eghball, B. Microbial quality of runoff following land application of cattle manure and swine slurry. J. Water Health 2005, 3, 157–171. [Google Scholar]
  60. Sistani, K.R.; Bolster, C.H.; Way, T.R.; Tobert, H.A.; Pote, D.H.; Watts, D.B. Influence of poultry litter application methods on the longevity of nutrient and E. coli in runoff from tall fescue pasture. Water Air Soil Pollut. 2010, 206, 3–12. [Google Scholar] [CrossRef]
  61. Singh, R.; Kim, J.; Marion, W.S., Jr.; Luo, F.; Jiang, X. Determining thermal inactivation of Escherichia coli O157:H7 in fresh compost by simulating early phases of the composting process. Appl. Environ. Microbiol. 2011, 77, 4126–4135. [Google Scholar] [CrossRef]
  62. Bernal, M.P.; Alburquerque, J.A.; Moral, R. Composting of animal manures and chemical criteria for compost maturity assessment. A review. Bioresource Technol. 2009, 100, 5444–5453. [Google Scholar] [CrossRef]
  63. Millner, P.D. Manure Managemen. In The Production Contamination Problem; Matthews, K., Solomon, E., Sapers, G., Eds.; U.S. Department of Agriculture (USDA): Beltsville, MD, USA, 2009; Volume 1, pp. 79–104. [Google Scholar]
  64. Barker, K.J.; Purswell, J.L.; Davis, J.D.; Parker, H.M.; Kidd, M.T.; McDaniel, C.D.; Kiess, A.S. Distribution of bacteria at different poultry litter depths. Int. J. Poult. Sci. 2010, 9, 10–13. [Google Scholar] [CrossRef]
  65. U.S. Department of Agriculture (USDA). Chapter 2, Composting. Part 637 Environmental Engineering, National Engineering Handbook; U.S. Department of Agriculture (USDA): Washington, DC, USA, 2000. [Google Scholar]
  66. Sweeten, J.M. Composting Manure and Sludge. In Proceedings of the National Poultry Waste Management Symposium, Columbus, OH, USA, 18–19 April 1988; Ohio State University: Columbus, OH, USA, 1988. [Google Scholar]
  67. Moore, P.A.; Daniel, T.C.; Edwards, D.R. Reducing phosphorus runoff and inhibiting ammonia loss from poultry manure with aluminum sulfate. J. Environ. Qual. 2000, 29, 37–49. [Google Scholar]
  68. Moore, P.A.; Daniel, T.C.; Gilmour, J.T.; Shreve, B.R.; Edwards, D.R.; Wood, B.H. Decreasing metal runoff from poultry litter with aluminium sulfate. J. Environ. Qual. 1998, 27, 92–99. [Google Scholar]
  69. Ryckeboer, J.; Mergaert, J.; Coosemans, J.; Deprins, K.; Swings, J. Microbiological aspects of biowaste during composting in a monitored compost bin. J. Appl. Microbiol. 2003, 94, 127–137. [Google Scholar] [CrossRef]
  70. Hassen, A.; Belguith, K.; Jedidi, N.; Cherif, A.; Cherif, M.; Boudabous, A. Microbial characterization during composting of municipal solid waste. Bioresour. Technol. 2001, 80, 217–225. [Google Scholar] [CrossRef]
  71. Erickson, M.C.; Liao, J.; Ma, L.; Jiang, X.; Doyle, M.P. Inactivation of Salmonella spp. in cow manure composts formulated to different initial C:N ratios. Bioresour. Technol. 2009, 100, 5898–5903. [Google Scholar] [CrossRef]
  72. Talaro, K.P.; Talaro, A. Physical and Chemical Control of Microbes. In Foundations in Microbiology, 4th ed.; The McGraw-Hill Companies: New York, NY, USA, 2002; pp. 325–326. [Google Scholar]
  73. U. S. Food and Drug Administration (USFDA). National Organic Standards Board Crops Committee Rcommendation for Guidance Use of Compost, Vermicompost, Processed Manure, and Compost Teas; U. S. Food and Drug Administration (USFDA): Silver Spring, MD, USA, 2006.
  74. U. S. Environmental Protection Agency (USEPA). Control of Pathogens and Vector Attraction in Sewage Sludge; U. S. Environmental Protection Agency (USEPA): Cincinnati, OH, USA, 2003.
  75. McCaskey, T.A. Dead Bird Composting; Auburn University: Auburn, AL, USA, 1993. [Google Scholar]
  76. Sims, J.T.; Murphy, D.W.; Handwerker, T.S. Composting of poultry wastes: Implications for dead poultry disposal and manure management. J. Sustain. Agric. 1993, 2, 67–82. [Google Scholar]
  77. Tiquia, S.M.; Tam, N.F.Y. Characterization and composting of poultry litter in forced-aeration piles. Process Biochem. 2002, 37, 869–880. [Google Scholar] [CrossRef]
  78. Brodie, H.L.; Donald, J.O.; Conner, D.E.; Tucker, J.K.; Harkin, H.D. Field evaluation of mini-composting of poultry carcasses. Poult. Sci. 1994, 73, 41. [Google Scholar]
  79. Macklin, K.S.; Hess, J.B.; Bilgili, S.F. In-house windrow composting and its effects on foodborne pathogens. J. Appl. Poult. Res. 2008, 17, 121–127. [Google Scholar] [CrossRef]
  80. Silva, M.E.; Lemos, L.T.; Cunha-Queda, A.C.; Nunes, O.C. Co-composting of poultry manure with low quantities of carbon-rich materials. Waste Manag. Res. 2009, 27, 119–128. [Google Scholar] [CrossRef]
  81. Guan, J.; Spencer, J.L.; Sampath, M.; Devenish, J. The fate of a genetically modified Pseudomonas strain and its transgene during the composting of poultry manure. Can. J. Microbiol. 2004, 50, 415–421. [Google Scholar] [CrossRef]
  82. Hutchison, M.L.; Walters, L.D.; Avery, S.M.; Moore, A. Decline of zoonotic agents in livestock waste and bedding heaps. J. Appl. Microbiol. 2005, 99, 354–362. [Google Scholar] [CrossRef]
  83. Erickson, M.C.; Liao, J.; Boyhan, G.; Smith, C.; Ma, L.; Jiang, X.; Doyle, M.P. Fate of manure-borne pathogen surrogates in static composting piles of chicken litter and peanut hulls. Bioresour. Technol. 2010, 101, 1014–1020. [Google Scholar] [CrossRef]
  84. Wichuk, K.M.; McCartney, D. A review of the effectiveness of current time-temperature regulations on pathogen inactivation during composting. J. Environ. Eng. Sci. 2007, 6, 573–586. [Google Scholar] [CrossRef]
  85. Wesche, A.M.; Gurtler, J.B.; Marks, B.P.; Ryser, E.T. Stress, sublethal injury, resuscitation, and virulence of bacterial foodborne pathogens. J. Food Protect. 2009, 72, 1121–1138. [Google Scholar]
  86. Shepherd, M.W.; Singh, R.; Kim, J.; Jiang, X. Effect of heat-shock treatment on the survival of Escherichia coli O157: H7 and Salmonella enteric Typhimurium in dairy manure co-composted with vegetable wastes under field conditions. Bioresour. Technol. 2010, 101, 5407–5413. [Google Scholar] [CrossRef]
  87. Farber, J.M.; Brown, B.E. Effect of prior heat shock on heat resistance of Listeria monocytogenes in meat. Appl. Environ. Microbiol. 1990, 56, 1584–1587. [Google Scholar]
  88. Berk, P.A.; de Jonge, R.; Zwietering, M.H.; Abee, T.; Kieboom, J. Acid resistance variability among isolates of Salmonella enterica serovar Typhimurium DT 104. J. Appl. Microbiol. 2005, 99, 859–866. [Google Scholar] [CrossRef]
  89. Johnson, K.M.; Busta, F.F. Detection and Enumeration of Injured Bacterial Spores in Processed Foods. In The Revival of Injured Microbes; Andrew, M.H.E., Russell, A.D., Eds.; Academic Press: London, UK, 1984; pp. 241–256. [Google Scholar]
  90. Rowe, M.T.; Kirk, R.B. Effect of nutrient starvation on the resistance of Escherichia coli O157:H7 to subsequent heat stress. J. Food Protect. 2000, 63, 1745–1748. [Google Scholar]
  91. Humphrey, T. Salmonella, stress response and food safety. Nat. Rev. 2004, 2, 504–509. [Google Scholar]
  92. Humphrey, T.J.; Williams, A.; McAlpine, K.; Lever, M.S.; Guard-Petter, J.; Cox, J.M. Isolates of Salmonella enterica Enteritidis PT4 with enhanced heat and acid tolerance are more virulent in mice and moreinvasive in chickens. Epidemiol. Infect. 1996, 177, 79–88. [Google Scholar]
  93. Foster, J.W.; Spector, M.P. How Salmonella survive against the odds. Annu. Rev. Microbiol. 1995, 49, 145–174. [Google Scholar] [CrossRef]
  94. Yousef, A.E.; Courtney, P.D. Basics of Stress Adaptation and Implications in New-Generation Foods. In Microbial Stress Adaptation and Food Safety; Yousef, A.E., Juneja, V.J., Eds.; CRC Press: Boca Raton, FL, USA, 2003; pp. 1–30. [Google Scholar]
  95. Abee, T.; Wouters, J.A. Microbial stress response in minimal processing. Int. J. Food Microbiol. 1999, 50, 65–91. [Google Scholar] [CrossRef]
  96. Suh, S.; Silo-Suh, L.; Woods, D.E.; Hassett, D.J.; West, S.E.H.; Ohman, D.E. Effect of rpoS mutation on the stress response and expression of virulence factors in Pseudomonas aeruginosa. J. Bacteriol. 1999, 181, 3890–3897. [Google Scholar]
  97. Cheville, A.M.; Arnold, K.W.; Buchrieser, C.; Cheng, C.M.; Kaspar, C.W. rpoS Regulation of acid, heat, and salt tolerance in Escherichia coli O157:H7. Appl. Environ. Microbiol. 1996, 62, 1822–1824. [Google Scholar]
  98. Van Hoek, A.H.A.M.; Aarts, H.J.M.; Bouw, E.; van Overbeek, W.M.; Franz, E. The role of rpoS in Escherichia coli O157 manure-amended soil survival and distribution of allelic variations among bovine, food and clinical isolates. FEMS Microbiol. Lett. 2013, 338, 18–23. [Google Scholar] [CrossRef]
  99. Ghaly, A.E.; Alhattab, M. Drying poultry manure for pollution potential reduction and production of organic fertilizer. Am. J. Environ. Sci. 2013, 9, 88–102. [Google Scholar] [CrossRef]
  100. Messer, J.W.; Lovett, J.; Murthy, G.K.; Murthy, G.K.; Wehby, A.J.; Schafer, M.L.; Read, R.B. An assessment of some public health problems resulting from feeding poultry litter to animals. Poult. Sci. 1971, 50, 874–881. [Google Scholar] [CrossRef]
  101. Chen, Z.; Diao, J.; Dharmasena, M.; Ionita, C.; Jiang, X.; Rieck, J. Thermal inactivation of desiccation-adapted Salmonella spp. in aged chicken litter. Appl. Environ. Microbiol. 2013, 79, 7013–7020. [Google Scholar] [CrossRef]
  102. National Organic Standards Board. Crops Committee Recommendation for Guidance Use of Compost, Vermicompost, Processed Manure, and Compost Teas; National Organic Standards Board: Washington, DC, USA, 2006.
  103. Commission Regulation (EC) No 208/2006 of 7 February 2006: Amending Annexes VI and VIII to Regulation (EC) No 1774/2002 of the European Parliament and of the Council as Regards Processing Standards for Biogas and Composting Plants and Requirements for Manure. Available online: (accessed on 8 January 2014).
  104. California Leafy Green Products Handler Marketing Agreement. Commodity Specific Food Safety Guidelines for the Production and Harvest of Lettuce and Leafy Greens; California Leafy Green Products Handler Marketing Agreement: Sacramento, CA, USA, 2010.
  105. Barbour, E.K.; Husseini, S.A.; Farran, M.T.; Itani, D.A.; Houalla, R.H.; Hamadeh, S.K. Soil solarization: A sustainable agriculture approach to reduce microorganisms in chicken manure-treated soil. J. Sustain. Agric. 2002, 19, 95–104. [Google Scholar]
  106. Oni, R.; Sharma, M.; Micallef, S.; Buchanan, R. The effect of UV radiation on survival of Salmonella enterica in dried manure dust. In Proceedings of the International Association for Food Protection Annual Meeting, Charlotte, NC, USA, 30 July 2013.
  107. Rothrock, M.J.; Cook, K.L.; Warren, J.G.; Sistani, K. The effect of alum addition on microbial communities in poultry Litter. Poult. Sci. 2008, 87, 1493–1503. [Google Scholar] [CrossRef]
  108. Gandhapudi, S.K.; Coyne, M.S.; D’Angelo, E.M.; Matocha, C. Potential nitrification in alum-treated soil slurries amended with poultry manure. Bioresour. Technol. 2006, 97, 664–670. [Google Scholar] [CrossRef]
  109. Scantling, M.; Waldroup, A.; Mary, J.; Moore, P. Microbiological effects of treating poultry litter with aluminum sulfate. Poult. Sci. (Abstr.) 1995, 74, 216. [Google Scholar]
  110. Line, J.E. Aluminum sulfate treatment of poultry litter to reduce Salmonella and Campylobacter populations. Poult. Sci. (Abstr.) 1998, 77, S364. [Google Scholar]
  111. Line, J.E. Campylobacter and Salmonella populations associated with chicken raised on acidified litter. Poult. Sci. 2002, 81, 1473–1477. [Google Scholar]
  112. U. S. Environmental Protection Agency (USEPA). Biosolids Generation, Use, and Disposal in the United States; U. S. Environmental Protection Agency (USEPA): Cincinnati, OH, USA, 1999.
  113. Stringfellow, K.; Caldwell, D.; Lee, J.; Byrd, A.; Carey, J.; Kessler, K.; Farnell, M. Pasteurization of chicken litter with steam and quicklime to reduce Salmonella Typhimurium. J. Appl. Poult. Res. 2010, 19, 380–386. [Google Scholar] [CrossRef]
  114. Hills, B.P.; Manning, C.E.; Ridge, Y.; Brocklehurst, T. Water availability and the survival of Salmonella typhimurium in porous systems. Int. J. Food Microbiol. 1997, 36, 187–198. [Google Scholar] [CrossRef]
  115. Maguire, R.O.; Hesterberg, D.; Gernat, A.; Anderson, K.; Wineland, M.; Grimes, J. Liming poultry manures to decrease soluble phosphorus and suppress the bacteria population. J. Environ. Qual. 2006, 35, 849–857. [Google Scholar] [CrossRef]
  116. Bennett, D.S.; Higgins, S.E.; Moore, R.; Beltran, R.; Caldwell, D.; Byrd, J.A.; Hargis, B.M. Effects of lime on Salmonella enteritidis survival in vitro. J. Appl. Poult. Res. 2003, 12, 65–68. [Google Scholar]
  117. Bennett, D.S.; Higgins, S.E.; Moore, R.; Byrd, J.A.; Beltran, R.; Corsiglia, C.; Caldwell, D.; Hargis, B.M. Effect of addition of hydrated lime to litter on recovery of selected bacteria and poult performance. J. Appl. Poult. Res. 2005, 14, 721–727. [Google Scholar]
  118. Turnbull, P.C.; Snoeyenbos, G.H. The roles of ammonia, water activity, and pH in the salmonellacidal effect of long-used poultry litter. Avian Dis. 1973, 17, 72–86. [Google Scholar] [CrossRef]
  119. Wang, G.; Zhao, T.; Doyle, M.P. Fate of enterohemorrhagic Escherichia coli O157:H7 in bovine feces. Appl. Environ. Microbiol. 1996, 62, 2567–2570. [Google Scholar]
  120. Ferguson, N.S.; Gates, R.S.; Taraba, J.L.; Cantor, A.H.; Pescatore, A.J.; Straw, M.L.; Ford, M.J.; Burnham, D.J. The effect of dietary protein and phosphorus on ammonia concentration and litter composition in broilers. Poult. Sci. 1998, 77, 1085–1093. [Google Scholar]
  121. Fontenot, J.P.; Webb, K.E.; Harmon, B.W.; Tucker, R.E.; Moore, W.E.C. Studies of processing nutritional value and palatability of broiler litter for ruminants. In Proceedings of the International Symposium on Livestock Wastes, Columbus, OH, USA, 19–22 April 1971.
  122. Caswell, L.F.; Fontenot, J.P.; Webb, K.E. Effect of processing treatment on pasteurization and nitrogen components of broiler litter and on nitrogen utilization by sheep. J. Anim. Sci. 1975, 4, 750–758. [Google Scholar]
  123. Seltzer, W.; Moum, S.G.; Goldhart, T.M. A method for the treatment of animal wastes to control ammonia and other odors. Poult. Sci. 1969, 48, 1912–1918. [Google Scholar] [CrossRef]
  124. Murray, G.E.; Tobin, R.S.; Junkins, B.; Kushner, D.J. Effect of chlorination on antibiotic resistance profiles of sewage-related bacteria. Appl. Environ. Microbiol. 1984, 48, 173–177. [Google Scholar]
  125. Munir, M.; Wong, K.; Xagoraraki, I. Release of antibiotic resistant bacteria and genes in the effluent and biosolids of five wastewater utilities in Michigan. Water Res. 2011, 45, 681–693. [Google Scholar] [CrossRef]
  126. Chen, Z.; Zhu, C.; Han, Z. Effects of aqueous chlorine dioxide treatment on nutritional components and shelf-life of mulberry fruit (Morus alba L.). J. Biosci. Bioeng. 2011, 111, 675–681. [Google Scholar] [CrossRef]
  127. Erickson, M.C.; Islam, M.; Sheppard, C.; Liao, J.; Doyle, M.P. Reduction of Escherichia coli O157:H7 and Salmonella enterica serovar Enteritidis in chicken manure by larvae of the black soldier fly. J. Food Protect. 2004, 67, 685–690. [Google Scholar]
  128. Yongabi, K.A.; Harris, P.L.; Lewis, D.M. Poultry faeces management with a simple low cost plastic digester. Afr. J. Biotechnol. 2009, 8, 1560–1566. [Google Scholar]
  129. Krylova, N.I.; Khabiboulline, R.E.; Naumova, R.P.; Nagle, M. The influence of ammonium and methods for removal during theanaerobic treatment of poultry manure. J. Chem. Technol. Biotechnol. 1997, 70, 99–105. [Google Scholar] [CrossRef]
  130. Heringa, S.D.; Kim, J.; Jiang, X.; Doyle, M.P.; Erickson, M.C. Use of a mixture of bacteriophages for biological control of Salmonella enteric strains in compost. Appl. Environ. Microbiol. 2010, 76, 5327–5332. [Google Scholar] [CrossRef]

Share and Cite

MDPI and ACS Style

Chen, Z.; Jiang, X. Microbiological Safety of Chicken Litter or Chicken Litter-Based Organic Fertilizers: A Review. Agriculture 2014, 4, 1-29.

AMA Style

Chen Z, Jiang X. Microbiological Safety of Chicken Litter or Chicken Litter-Based Organic Fertilizers: A Review. Agriculture. 2014; 4(1):1-29.

Chicago/Turabian Style

Chen, Zhao, and Xiuping Jiang. 2014. "Microbiological Safety of Chicken Litter or Chicken Litter-Based Organic Fertilizers: A Review" Agriculture 4, no. 1: 1-29.

Article Metrics

Back to TopTop