1. DUNGTREAT
CATTLE DUNG PROCESSING
In the last few decades livestock practices have evolved considerably. Highly integrated
farms, notably in cattle (Bos taurus), pig (Sus scrofa), and poultry production, have
largely disappeared, replaced by intensive systems using confined rearing methods.
Management of the large volumes of excreta produced from these systems has meant
bedding is minimized and slatted floors are employed, allowing feces and urine to
collect as slurry containing approximately 3 to 12% solids. As intensive farming methods
have proven economically effective, many adverse effects of handling livestock wastes,
particularly as slurry, have become evident. The main problems were summarized by
Pain et al. (1987):
(i) Ammonia volatilization.
(ii) Offensive odor release.
(iii) Handling problems due to the formation of crusts and sediments during storage.
In addition, other issues, such as the pollution of watercourses via surface runoff and
the spread of pathogens, are becoming ever-increasing concerns. The importance of all
these problems varies according to the nature of the waste, concerns of the farmer,
distance of neighbors, vulnerability of the surrounding environment, and current
legislation.
One of the most promising methods of disposal of cattle manure, is recycling as a
livestock feed ingredient.
Concentrate-fed animals excrete more digestible crude fiber in their feces than cattle
fed high-roughage diets
(Mc-Clure et al., 1971; Lucas et al., 1975; Newton et al., 1977).

2. Nutrient concentration Range in Solid Beef manure.
(Lb/ tonne)
Nitrogen (N) 7-36
Phosphorus (P) 2-6
Potassium (K) 7-17
Sulphur (S) 0.1-3
Note: multiply P by 2.3 to get P2O5 and K by 1.2 to get K2O
Adapted from Schoenau , 1997
Dried Cow dung contains 3290 Kcal/kg Calorific value
TYPICAL CHEMICAL COMPOSITION OF CATTLE MANURE
Dry matter, % 26.6
Dry matter basis
Crude protein, % 11.9
Crude fiber, % 50.9
NFE, % 31.6
Ether extract, % 0.2
Ash, % 5.4
Calcium, % 0.63
Phosphorus, % 0.17
Gross energy, Mcal/kg 4.61
Iron, ppm 612
Copper, ppm 12
Nickel, ppm 6
Cadmium, ppm 0.76
Lead, ppm 1
Mercury, ppm . 0.07
Present technology provides a wide array of innovative treatments for managing
livestock wastes. Among these, the majority of research has concentrated on biogas
(methane) production, anaerobic and/or aerobic purification, and solids separation.
While these methods have proven effective (Woestyne and Verstraete, 1995), their use

3. is limited, primarily due to the high cost and expertise required to operate these
mechanized systems effectively.
AMMONIA EMISSIONS
Livestock slurry is a valuable fertilizer source for crop production but its value is reduced
over time by significant losses of nitrogen (N), attributed mainly to the volatilization of
NH3
(Lauer et al., 1976; Pain et al., 1987; Hartung and Phillips, 1994).
In addition to the economic loss, NH3 emission and subsequent deposition can be a
major source of pollution, causing N enrichment, acidification of soils and surface
waters, and the pollution of ground and surface waters with nitrates
(Hartung, 1992; Sutton et al., 1995; Pain et al., 1998).
In the housed environment, NH3 emissions can also adversely affect the health,
performance, and welfare of both animals (Donham, 1990) and human attendants
(Donham et al., 1977; Donham and Gustafason, 1982).
During the last 30 years NH3 emissions in Europe have increased by more than 50%
(ApSimon et al., 1987; Sutton et al., 1995).
Intensification in livestock production has been identified as the primary contributor to
this increase and is estimated to account for 80% of yearly emissions
(Buijsman et al., 1987; Pain et al., 1998).
Consequently, many European countries have implemented legal constraints on the
spreading of livestock slurry (Burton, 1996), necessitating an increase in storage
capacity.
Storage of livestock slurry has been recognized as a major source of NH3 emissions
(Hartung and Phillips, 1994), with reported N losses ranging from 3 to 60% of initial total
N
(Muck and Steenhuis, 1982; Dewes et al., 1990).

4. Factors Influencing Volatilization
The concentration and type of N in livestock slurry varies according to animal species,
diet, and age.
Typically, livestock use less than 30% of N contained in their feed, with 50 to 80% of the
remainder excreted in the urine and 20 to 50% excreted in the feces. Urea is the major
nitrogenous component in urine, accounting for up to 97% of urinary N.
The exception is poultry manure, where uric acid is excreted instead of urea.
Urea is hydrolyzed by the enzyme urease, found in the feces, to ammonium (NH+4) and
bicarbonate ions.
Hydrolysis occurs rapidly, with complete conversion of urea N to NH+4 possible within a
matter of hours, depending on environmental conditions
(Muck and Richards, 1980; Beline et al., 1998).
Fecal N typically consists of 50% protein N and 50% NH+4. Mineralization of fecal protein
N mainly occurs through the activity of proteolytic and deaminative bacteria, initially
hydrolyzing proteins to peptides and amino acids and finally by deamination to NH+4.
This process occurs at a far slower rate than the hydrolysis of urea and is thought to be a
relatively unimportant source of NH+4 where livestock slurry is stored for a short period
of time
(Muck and Steenhuis, 1982).
However, where livestock slurry is stored for long periods, especially at higher
temperatures, it becomes the dominant pathway for NH+4 production
(Patni and Jui, 1991).
Reactions that govern NH3 volatilization may be represented by the following
summarized equation
(Freney et al., 1981):
[1]

5. The driving force for NH3 volatilization is considered to be the difference in NH3 partial
pressure between that in equilibrium with the liquid phase and that in the ambient
atmosphere. In the absence of other ionic species, this is predominately influenced by
the NH+4 concentration, pH, and temperature, although any displacement of the
equilibrium will affect NH3 emission.
OFFENSIVE ODORS
Offensive odor emanating from livestock production is of concern for intensive systems
and confined operations as the number of complaints continue to rise
(Jongebreur, 1977; O'Neill and Phillips, 1991; Misselbrook et al., 1993).
Odors from livestock slurry are due to a complex mixture of volatile compounds arising
from anaerobic degradation of plant fiber and protein
(Spoelstra, 1980; Hammond, 1989).
Chemical analysis has identified approximately 170 volatile compounds
(Spoelstra, 1980; Yasuhura et al., 1984; O'Neill and Phillips, 1992).
According to O'Neill and Phillips (1992), the most important odorous components
emitted from livestock slurry appear to be the volatile fatty acids (VFAs: p-cresol, indole,
skatole, hydrogen sulfide, and NH3), by virtue of either their high concentrations or their
low odor thresholds.
Odor can be assessed by two criteria: strength, which is measured as concentration or
intensity, and offensiveness (i.e., the perceived quality). Relationships between the
known volatile compounds and perceived olfactory responses have also been sought by
many researchers
(e.g., Schaefer, 1977; Williams, 1984; Pain et al., 1990; Mackie, 1994; Zhu et al., 1997b).
At present, though, no compound has been found suitable as a marker to predict
olfactory response. Based on olfactory measurements, the problem of odor nuisance
can be tackled by reducing either the perceived strength or offensiveness

6. (O'Neill and Phillips, 1991).
Reducing odor strength implies destroying or diluting odorants, whereas reducing odor
offensiveness implies modifying odorants emitted from livestock slurry.
Handling Properties
Where livestock waste is handled as a slurry, handling problems are often encountered
due to the formation of crusts and sediments during storage that make removal for
timely and accurate applications to land difficult
(Pain et al., 1987).
The rheological properties of a livestock slurry are dependant on its total solids content
(Chen, 1986).
Reducing total solids reduces viscosity and so reduces power and cost when pumping.
The composition of solids varies considerably among animal species, age, physiological
state, and diet, but generally consist of undigested plant fiber and protein.
Stimulating the microbial degradation of total solids would appear to be a more feasible
application than either control of NH3 or odor emissions, as the targeted organic
compounds are readily identified.
Work is needed to discover the microbial decay patterns of theses organic compounds
in livestock slurries and identify the responsible enzymes and bacterial genera.
Pollution to Surface Watercourses
Today there is considerable pressure on farmers to avoid water pollution.
On entry to a watercourse, livestock wastes exert a high biochemical oxygen demand
(BOD) and cause eutrophication due to high levels of nutrients, particularly N and
phosphorous (P).

7. Williams (1983) found that the volatile fatty acid (VFA) fraction of livestock slurry
accounted for up to 70% of its BOD.
The VFA fraction of livestock wastes has also been identified as a primary contributor to
odor
(Zhu et al., 1997c; Mackie et al., 1998; Zhu and Jacobson, 1999; Zhu et al., 1999).
Enhancing the degradation of this fraction reduction may well also lower the BOD.
However, further understanding of the microbiology pathways in livestock wastes is
required before this can be achieved.
Phosphorus runoff from land receiving slurry is another major environmental problem,
particularly from sites receiving poultry manure.
The majority of P runoff is from the dissolved reactive P fraction.
Pathogens
Many of the bacteria in livestock slurry are pathogenic and pose a heath risk.
DUNGTREAT
Present method is to treat and biodegrade the cattle dung so as odour is controlled,
pathogens are eliminated by compettion and the material is biodegraded to form
assimable nutrients for use in plants in the first phase.
1.5 Kg/Ton dung once uniformly spread over layers of each not exceeding 12.5 cm
height and total heap not exceeding 45 cm height.
Moisture is to be maintained @50% level upto 40 days.
Treatment completes in about 45 days.
In the later phases, efforts can be made to convert this biodegraded material fit for
animal consumption as a feeding stuff in the concentrate feeds @ 10% replacing the de
oiled rice or wheat brans.

8. DIGESTION COEFFICIENTS AND TDN OF DIETS AND MANURE ROUGHAGE
Diets: Untreated Manure roughage as fed Manure roughage
Digestibility, % 0 20% 40% 60% SE a Sign. b Mean c SEd
Dry matter 68.3 62.0 58.9 50.3 2.7 P<.001 23.0 3.3
Crude protein 57.5 54.8 50.0 41.7 2.1 P<.01 10.7 2.5
Crude fiber 29.4 31,1 33.9 31.9 5.2 N.S. 39.4 5.0
NFE 77.6 72.5 69.4 61.3 2.3 P<.O01 36.8 2.9
Ether extract 83.8 77.5 87.2 83.9 4.8 N.S. 101.2 5.3
Gross energy 64.6 59.9 57.9 49.6 3.0 P<.01 29.2 3.5
TDN 73.5 64.6 62.2 52.2 3.0 P<.001 33.0 3.8
apooled standard error of mean, n = 4.
bsignificance level of linear term of manure roughage dry matter in model (quadratic
and cubic terms, N.S.).
CCalculated by method of Kromann (1967) and Kromann et al. (1977).
dstandard error of regression, n = 16.
DIGESTIBLE AND METABOLIZABLE ENERGY AND NITROGEN VALUES OF
DIETS
Manure roughage as fed
Item 0 20% 40% 60%
SEa Significance b
Digestible energy c,
Mcal/kg,
dry weight 2.99 2.70 2.69 2.29 .14 P<.01
Metabolizable energy c
Mcal/kg, dry weight 2.59 2.33 2.35 1.98 .13 P<.O1
Percentage of gross energy lost as:
Fecal energy, % 35.4 41.1 42.1 50.4 3.02 P<.O1
Methane energy, % 6.2 5.7 5.3 4.7 .27 N.S.

9. Urine energy, % 2.5 2.4 1.8 1.9 .24 N.S.
Nitrogen data, daily basis:
N intake, g 153.9 162.0 190.0 166.1 8.34 N.S.
Fecal N, g 65.3 73.6 94.9 97.0 5.92 P<.O1
Urinary N, g 56.4 55.5 46.6 37.5 4.54 P<.O01
N balance, g 32.2 32.9 48.5 31.6 5.67 N.S.
N balance as % of N intake 20.9 20.3 25.5 19.0 7.00 N.S.
N balance as % of N digested 35.2 37.5 51.1 44.0 4.89 P<.05
A standard error of the mean, n = 16.
bsignificance of linear term of manure roughage dry matter (quadratic, cubic and
interaction terms, N.S.).
CDE and ME values for the manure roughage when calculated by the method of
Kromann (1967)and Kromann et aI. (1977) were 1.35 and 1.21 Mcal/kg dry weight,
respectively.
EFFECT OF MANURE ROUGHAGE IN FEEDLOT DIETS FED STEERS
ON ENERGY UTILIZATION, NEm and NEg VALUES, 124 DAYS
Manure roughage in diets, % as fed 0 O 20 20 40 40 60 60
Feed intake, % of ad libitum 50 100 50 100 50 100 50 100
Avg metabolic size, W~g J 70.6 75.4 72.3 80.7 73.5 81.3 71.9 79.8
ME in feed, Mcal/kg d. wt 2.59 2.59 2.33 2.33 2.35 2.35 1.98 1.98
ME intake/steer/day,Meal 10.85 20.03 11.25 21.62 12.69 23.59 11.03 20.36
Heat production, Meal/steer/day 10.18 16.58 10.32 16.87 10.62 18.75 9.56 15.53
NEm heat production, Meal/steer/day a 5.51 5.89 5.65 6.30 5.74 6.35 5.61 6.23
Heat increment, Meal/steer/day 4.67 10.69 4.67 10.57 4.88 12.40 3.95 9.30
Total heat/ME intake, % 93.8 82.8 91.7 78.0 83.7 79.5 86.7 76.3
Heat increment/ME intake, % 43.0 53.4 41.5 48.9 38.5 52.6 35.8 45.7
NE m heat/ME intake, % 50.8 29.4 50.2 29.1 45.2 26.9 50.9 30.6
Energy balance/ME intake, % 6.2 17.2 8.3 22.0 16.3 20.5 13.3 23.7
NE m of diet, Mcal/kg b 1.55 1.55 1.46 1.46 1.51 1.51 1.30 1.30

10. NEg of diet, Mcal/kg c 1.060 .875 .970 .959 1.308 .833 1.168 .879
a
78.08 kcal/W'k75 X avg metabolic size, W~g.
b
NEm, Mcal/kg = Energy required for maintenance, Meal/day (Vance et al.,
1972)
Dry matter intake at energy equilibrium, kg/day
C
NEg, Mcal/kg = Energy retained in tissues, Mcal/day
Total dry matter intake-dry matter intake at energy equilibrium, kg/day
(Vance et al., 1972)
DUNGTREAT CONTAINS
Nitrifying Bacteria, Herbal Gas adsorbants, Deodourants, Enzymes, Probiotics, Osmo
Regulators, Methyl Donors, Uni Cellar Protein Producing Microorganisms, Amino acid
producing Microorganisms.
SUGGESTED LEVEL AND METHOD OF USAGE:
USE @ 2 Kg/ MT dung ( Heap height not exceeding 9 inches) ( Maintain 35-40%
Moisture Level for 10 Days) (Room temperature). Once in a day give the heap a turning
for the first 10 Days.
Treatment time: 10 + 4 Days
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