CARBON DIOXIDE AND AMMONIA EMISSION DURING CO … Issue... · Co-Composting of Organic Fraction of Municipal Solid Waste and Brewery Sludge Contact Us : [email protected] ; ... Where

International Journal of Advances in Engineering & Scientific Research, Vol.3, Issue 5, Nov - 2016,

pp 09-28 ISSN: 2349 –3607 (Online) , ISSN: 2349 –4824 (Print)

Contact Us : [email protected] ; submit paper : [email protected] download full paper : www.arseam.com 9

www.arseam.com

CARBON DIOXIDE AND AMMONIA EMISSION

DURING CO-COMPOSTING OF ORGANIC FRACTION

OF MUNICIPAL SOLID WASTE AND BREWERY

SLUDGE

Hema Nalini. A.V*,

Dr. P.R. Sreemahadevan Pillai** & Dr. Y.V.K.S. Rao***

(* Research Scholar, University of Kerala, ** Dean-Faculty of Engineering, University of

Calicut, *** Research Guide, University of Kerala)

Abstract:

Carbon dioxide (CO2) and ammonia (NH3) are the two main gases emitted as a result of aerobic

biological composting. CO2 is a green house gas and NH3 can produce odour problem. CO2

emission can reduce the carbon (C) content and NH3 emission can reduce the nitrogen (N)

content in the final compost. In this study, the influence of brewery sludge, amendments, C/N

ratio, starting culture and aeration rate on the percentage losses of C and N in terms of CO2 and

NH3 respectively are experimented using Taguchi’s L8 orthogonal array with two replications.

An in-vessel reactor with forced aeration system using synthetic organic fraction of municipal

solid waste (OFMSW) and brewery sludge (BS) with provision for trapping CO2 and NH3 was

used. The analysis of the results show that the most significant factors influencing the reduction

in the loss of C as CO2 were amendment (coconut pith) and C/N ratio and in reducing the loss of

N as NH3 was the interaction between BS and coconut pith.

Keywords: carbon dioxide, ammonia, co-composting, OFMSW, BS

1. Introduction

Composting is the biological decomposition and stabilization of solid organic substrates, under

conditions that allow development of thermophilic temperatures as a result of biologically

produced heat, to produce a final product that is stable, low in moisture, free of pathogens and

plant seeds and can be beneficially applied to land. Co-composting is the process of enhancing

the composting by increasing the degradation rate and the quality of the compost, by

modifications such as addition of biodegradable wastes (industrial and domestic waste, sludge

etc.) to reach an optimum C/N ratio. Two major by-products of microbial transformation during

biodegradation of solid waste are CO2 and NH3. CO2 is a greenhouse gas, while NH3 is a

noxious, toxic gas that can cause serious damage to human health and to the environment (Cheng

C.Y. et. al., 2010). The emission of CO2 and NH3 can result in the loss of C and N respectively.

Volatilisation of NH3 greatly reduces the fertilizer value of the compost (de Guardia A. et. al.,

2010). Therefore, it is important that studies be carried out to find the quantities of these gases

mailto:[email protected]


Hema N.A.V , Sreemahadevan P.P.R & Rao Y.V.K.S / Carbon Dioxide and Ammonia Emission During

Co-Composting of Organic Fraction of Municipal Solid Waste and Brewery Sludge


and the factors influencing their emission. CO2 emission from composting facilities is biogenic

as a result of biological degradation of the organic matter, mostly as a consequence of aerobic

decomposition and to a lesser extent, from anaerobic processes or the oxidation of methane

(CH4) by aerobic methanotrophic bacteria. This emission accounts for the highest amount of gas

generated during the process, since between 40 and 70 % of the original organic matter can be

degraded during composting (Haug R.T., 1993). CO2 emission is an index of the overall

microbial activity in the process, reflecting the progress (Hobson A. et. al., 2005; Sánchez A. et.

al., 2015) and the evaluation of the stability of the end product. Temperature, pH value, C/N ratio

and aeration rate influence volatilization of NH3 during composting (Jiang T., et. al., 2011).

Here, in the processes taking place during co-composting of OFMSW and brewery sludge, the

emission of CO2 and NH3 using batch scale in-vessel composting system will be investigated in

the study. The composting process diagram is shown in Fig 1.

Fig 1. Composting Process Diagram

Materials and methods:

L8 (27) orthogonal array as prescribed by Taguchi was adopted to carry out the experimental

design with 5, 2-level factors with interaction among the factors AB and AC. The levels of

brewery sludge and C/N ratio were based on the micro-composting study (Hema Nalini et. al.,

July 2015) and for other factors based on the previous studies (Xueling Sun, 2006). Minitab 17

software was used for creating the design and is presented in Table1.

Table 1. Taguchi orthogonal array design with factor and factor notation Trial A

Brewery sludge

(%)

B

Amendment

C

C/N

D

Starting

culture

E

Aeration rate (L/min)

1 20 Cow dung 15 Without 3

2 20 Cow dung 30 With 4.5

3 20 Coconut pith 15 With 4.5

4 20 Coconut pith 30 Without 3

5 30 Cow dung 15 Without 4.5

6 30 Cow dung 30 With 3

7 30 Coconut pith 15 With 3

8 30 Coconut pith 30 Without 4.5






Reactor for in-vessel composting of 10 kg of substrate by wet weight with forced aeration system

and accessories for purifying, humidifying, stabilizing and controlling the inlet air was designed.

The reactor is of 300 mm inside diameter, 600 mm height and 6.5 mm thickness, with transparent

acrylic material. It is covered by 4 layers of heat insulation materials – aluminium foil of 0.056

mm thickness, felt of 5 mm thickness, asbestos coated winding rope of 6.5 mm thickness and

thermocol of 20 mm thickness in three layers to prevent heat loss. An aquarium pump of variable

speed type electric motor with inverter fitting and rating of 0-80 Lit/min was used for aeration.

The air is then passed through 1000 mL flask containing 2N KOH to capture ambient CO2 gas

and then passed through the humidifier which is containing distilled water and after that through

a humidity stabilizer containing activated carbon. The air is then admitted to an air chamber 12.7

mm x 12.7 mm x 9.5 mm by means of a PVC pipe, with air holes of 5.5 mm diameter, 2 numbers

each on the four faces. The air is then distributed to the compost matrix through a porous plate

from the air chamber. The exhaust gases from the compost unit is then passed through activated

carbon (coconut charcoal) trap to remove any volatile organic material that could interfere with

the estimation of CO2 and NH3. The condensate produced during the experiment was collected

using a condenser flask provided ahead of CO2 trap. The exhaust gas was then passed through a

500 mL, 5M KOH solution to capture CO2 and then through a 500 mL, 1N H2SO4 solution to

capture NH3 (Robert K. Ham and Dimitris Komilis, 2003). An empty sealed jar was kept between

the two traps to prevent overflow from the alkaline to the acidic solution. The experimental setup

is shown in Fig 2.

(a): schematic diagram

Fig 2: Experimental setup






(b): photograph

Estimation of CO2 evolved

The CO2 evolved and absorbed in an Erlenmeyer flask with 5M KOH solution was titrated

against 0.5N H2SO4 with phenolphthalein indicator. The following equation is used for

calculating the CO2 evolved.

CO2 = [(B – V) x N x E x Tr / A] / (w x (1-mc) x VS) ------(1)

Where: CO2 = carbon dioxide evolved [mg CO2-C/gm of VS]; B = volume of acid needed to

titrate the blank to the end point [ml]; V = volume of acid needed to titrate the sample to the end

point [ml]; N = normality of acid used for titration; E = equivalent weight to convert to mg [6 for

C]; Tr = trapped volume [ml]; A = aliquot titrated [ml]; w = sample weight [g]; mc = sample

moisture content; VS = volatile solids content in the sample [decimal dry basis] (Samy S.

Sadaka, et.al., 2006)

Estimation of NH3 Nitrogen

The ammonia N concentration can be determined by the Indophenol Blue Method (Keeney D.R.

and Nelson D.W., 1982). A variable wavelength spectrophotometer (UV-VIS SL 210 Elico),

equipped with 1 cm light path and capable of absorbance measurements at 636 nm was used. NH3 gas evolved can be computed using equation (2).

NH3 gas in mg/Kg of dry compost = 10 x (C1 x D1 x V) / (1-mc) ………(2)

Where C1 = concentration of NH3 in mg/L, D1 = dilution ratio, V = trapped volume in mL






SN Ratio Analysis

After conducting the experiment for 2 replications of 8 trials each, the responses are represented

as the percentage loss of C as CO2 and loss of N as NH3 and are analyzed by means of

calculating the SN ratio. Taguchi uses the SN ratio analysis to measure the quality characteristics

deviating from the desired value (Ranjit Roy, 1990). In SN ratio, the term ‘signal (S)’ represents

the desirable value (mean) for the output characteristic and the term ‘noise (N)’ represents the

undesirable value for the output characteristic. In general, a better signal is obtained when the

noise is smaller, so that a larger SN ratio gives better final result. That means, the divergence of

the final results becomes smaller. Depending upon the goal to be achieved for the responses, the

goal options can be selected and the corresponding equations can be used for SN analysis. For

the quality of processes or products when the responses are to be minimised, use smaller the

better criterion. The software Minitab 17 is equipped with facilities for doing the analysis for

various quality criteria. Equation (3) is used for computing SN ratio for smaller the better

criterion.

------(3)

Where Y is the response and ‘n’ is the number of tests in a trial.

The level of a factor with the highest SN ratio is the optimum level for responses measured. The

higher the SN ratio, the more favourable is the effect of input variable on the output. Here the

loss of C as CO2 and loss of N as NH3 are considered as the quality characteristics.

Preparation of substrate

The substrates used for the composting were synthetic Organic Fraction of Municipal Solid

Waste (OFMSW) (Hema Nalini A.V., et. al., April 2015, 2) and dewatered Brewery Sludge

(Hema Nalini A.V., et. al., April 2015, 1). Use of synthetic waste in composting studies enables

repeatability and reproducibility of the experiments. Simulated waste in experiments will give a

true picture of the behaviour of the original waste. The sludge from the brew-house of United

Breweries Ltd., Kanjikode, Kerala, was collected using the composite sampling technique.

Compost recipe can be prepared for a given quantity of synthetic waste by knowing C, N and mc

of each component in it. Once the C, N and mc of the components of substrates are known by

choosing the right material and adjusting the weights, the compost recipe can be prepared for a

given value of total weight, C/N ratio and mc, which can be done with the help of an Excel

spread sheet. Table 2 shows the weights of raw materials in kg for the trials 1 to 8 for two

replications R1 and R2.






Table 2: The weights of items in substrate for the experimental trials

The mc and the maximum particle size of the substrate were 70% and 5 mm respectively.

Running experiments

The random orderings for running the experiments is available (Robert. H.L. and Joseph. E.M.,

1990) in 200 different random combinations for 8-run experiment. One among the random

combination chosen here is 2, 7, 3, 6, 5, 8, 4, 1. The experiments were run as per this order. The

contents in the reactor were mixed daily using a hoe fork. The C ( Mylavarapu, R., 2009), N (IS:

10158, 1982), CO2 evolved (Samy S. Sadaka, et.al., 2006), NH3 evolved (Keeney D.R. and

Nelson D.W., 1982) and pH (IS: 10158, 1982) were monitored at 2 days interval and

temperature was monitored at 2 hours interval during the active phase of composting and at 4

hours interval during the cooling phase.

Results and discussion

The initial C/N ratio of composting substrate for trials 1, 3, 5 & 7 is 15 and for 2, 4, 6 & 8 it is

30. Therefore the % of C content of the trials with C/N 15, the initial C content of the substrate is

less compared to the trials with C/N 30. The initial N content of the substrate with C/N 15 is

more compared to the trials with C/N 30. Due to the oxidation of organic matter by

microorganisms, CO2 is produced which leads to the reduction in % of C with composting. On

the other hand the % of N content in the substrate is increasing with composting because of the

large % of removal of C as CO2. Fig 3 and Fig 4 show the temporal variation of % of C for trials

1 to 8 for replication 1 and 2 respectively and can be seen that the C content decrease with days

ITEM

Trial 1 Trial 2 Trial 3 Trial 4 Trial 5 Trial 6 Trial 7 Trial 8

R1 R2 R1 R2 R1 R2 R1 R2 R1 R2 R1 R2 R1 R2 R1 R2

Boiled rice 1.40 1.45 1.20 1.20 1.05 1.05 1.35 1.40 1.08 1.10 1.40 1.40 1.10 1.20 1.40 1.40

Pumpkin 0.80 0.75 1.60 1.50 0.68 0.52 1.85 1.80 1.30 1.30 1.65 1.50 0.25 0.34 1.30 1.20

Potato 0.60 0.60 0.40 0.40 0.70 0.76 0.30 0.30 0.45 0.40 0.15 0.15 0.47 0.50 0.30 0.35

Green

Banana

0.80 0.80 0.30 0.40 0.80 0.90 0.30 0.30 0.40 0.43 0.10 0.15 0.85 0.85 0.35 0.40

Papaya 2.20 2.20 0.00 0.00 2.40 2.40 0.00 0.00 1.90 1.90 0.00 0.00 2.02 1.90 0.00 0.00

Orange 0.00 0.00 2.20 2.20 0.00 0.00 2.10 2.10 0.00 0.00 1.80 1.90 0.00 0.00 2.00 2.00

Newspaper 0.50 0.50 0.50 0.50 0.47 0.47 0.50 0.50 0.47 0.47 0.45 0.45 0.41 0.41 0.45 0.45

Dry leaves 0.00 0.00 0.70 0.75 0.00 0.00 0.80 0.80 0.00 0.00 0.75 0.75 0.00 0.00 0.85 0.85

Grass

clippings

0.50 0.50 0.30 0.25 1.10 1.10 0.00 0.00 0.00 0.00 0.00 0.00 0.50 0.45 0.00 0.00

Green

leaves

0.80 0.80 0.00 0.00 0.00 0.00 0.40 0.40 1.05 1.05 0.00 0.00 0.70 0.65 0.00 0.00

Brewery

sludge

1.90 1.90 1.80 1.80 1.80 1.80 1.90 1.90 2.85 2.85 2.70 2.70 2.70 2.70 2.85 2.85

Cow dung 0.50 0.50 0.50 0.50 0.00 0.00 0.00 0.00 0.50 0.50 0.50 0.50 0.00 0.00 0.00 0.00

Coconut

pith

0.00 0.00 0.00 0.00 0.50 0.50 0.50 0.50 0.00 0.00 0.00 0.00 0.50 0.50 0.50 0.50

Unmatured

Compost

0.00 0.00 0.50 0.50 0.50 0.50 0.00 0.00 0.00 0.00 0.50 0.50 0.50 0.50 0.00 0.00






of composting and become stable at the end of composting. Fig 5 and Fig 6 show the variation

of % of N for trials 1 to 8 for replication 1 and 2 respectively.

Fig 3: Temporal variation of C for trials 1 to 8 for replication 1

Fig 4: Temporal variation of C for trials 1 to 8 for replication 2






Fig 5: Temporal variation of N for trials 1 to 8 for replication 1

Fig 6: Temporal variation of N for trials 1 to 8 for replication 2

As seen from the process diagram, due to the decomposition of the organic matter, heat is

produced, which can cause a rise in temperature that favors the thermophillic decomposition. Fig

7 to Fig 14 represent the temporal variation of temperature, pH, CO2 and NH3 evolved of two

replications for trials 1 to 8. For all the trials and replications it can be seen that the temperature

rapidly increased during the initial stages, reached peak values at which for most of the trials

CO2 production was maximum. The pH value during the initial days decreased for all the

replications and trials because of the production of CO2 and gradually increased due to the

production of NH3. Towards the end of composting the pH gradually decreased due to the

decreased production of NH3. For trials 2 and 5 of replication 1, the emission of CO2 was

fluctuating, which may be due to noise factors.






Fig 7: Variation of pH, NH3, CO2 and Temperature with time for trial 1


















Fig 15 and Fig 16 show respectively the cumulative CO2 evolved for replications 1 and 2 for

various trials with composting time. From the graphs, it is clear that the emission of CO2 is more

during the initial stages because the carbonaceous materials are readily oxidized; but towards the

end of composting the emission decreased due to the lower availability of easily fermentable

organic matter (Chiumenti A. et. al., 2007). Fig 17 and Fig 18 represent the cumulative emission

of NH3 for replications 1 and 2 respectively for all the trials with composting time. The emission

of NH3 was more in most of the trials at the end of the thermophillic phase. In the cooling phase,






the release and volatilization of NH3 is less and at the final stage of composting, N is bound to

complex organic molecules and involved in humification processes (Baddi G.A. et. al., 2004).

Fig 15: Cumulative CO2 produced with time for trials 1 to 8 of replication 1

Fig 16: Cumulative CO2 produced with time for trials 1 to 8 of replication 2

Fig 17: Cumulative NH3 produced with time for trials 1 to 8 of replication 1






Fig 18: Cumulative NH3 produced with time for trials 1 to 8 of replication 2

The CO2 and NH3 evolved can respectively reduce the C and N content of the compost.

Therefore the % of C loss as CO2 and N loss as NH3 were computed in terms of the initial C and

N respectively for the two replications for all the trials and kept as the responses for SN analysis

as shown in Table 3. SN analysis for smaller the better criteria was done to find the optimal

levels of factors in reducing the % of C as CO2 and N as NH3 during composting.

Table 3: Factors and responses for SN analysis Trial A

(BS, %)

B

(AM)

C

(C/N)

D

(SC)

E

(AR, L/min)

% of C loss as CO2

gas % of N loss as NH₃

gas

R1 R2 R1 R2

1 20 CD 15 WO 3 55.18 56.58 16.364 13.825

2 20 CD 30 W 4.5 30.89 31.01 16.102 16.692

3 20 CP 15 W 4.5 35.62 31.39 3.522 3.412

4 20 CP 30 WO 3 23.57 26.98 7.190 7.021

5 30 CD 15 WO 4.5 39.45 43.30 4.385 4.056

6 30 CD 30 W 3 32.40 31.61 19.427 18.675

7 30 CP 15 W 3 40.92 47.79 16.561 17.345

8 30 CP 30 WO 4.5 22.14 22.83 17.549 15.788

Note: AM is amendment, SC is starting culture, AR is aeration rate, W is with & WO is without

Optimization for C loss as CO2

The % of C loss as CO2 gas for two replications for the 8 trials was analysed for SN ratios for

smaller the better characteristic. The response table for SN ratios is given in Table 4 for all the

levels of factors without pooling. In the response table, Delta is the difference between SN ratios

between the levels of factors, which gives the rank of influencing factors in reducing the C loss






as CO2. Fig 19 represents the main effect plot for SN ratios of the loss of C as CO2 and the levels

of factors that gives maximum SN ratio is selected and it is A2B2C2D1E2 for the major

contributing factors. Fig 21 represents the interaction plot for SN ratios between BS and C/N

ratio. Since the contribution of interaction between BS and C/N

ratio is very less in reducing the loss of C as CO2, this interaction effect is pooled. This pooling

gives an error degree of freedom 1. Therefore in the subsequent analysis, this interaction is

eliminated. From Fig 20 it is clear that the factor levels for interaction between MS and

amendment is A1B2. The optimal levels of factors that can yield less C loss as CO2 is

A1B2C2D1E2, considering the main effects and interaction effects. In order to know the factor

contribution and the significance of the factors on total composting time, analysis of variance is

done and the results are presented in Table 5. From the table it is clear that the most significant

factor influencing in reducing the loss of C as CO2 is amendment and C/N ratio (p ˂ 0.05).

Coconut pith as amendment is effective in reducing the C loss as CO2. The % contributions of

factors and error are shown in the last column of Table 5 and are represented by a pie diagram in

Fig 22. The contribution of C/N is maximum and it is 65.46%.

Fig 19: Main effect plot for SN ratios of C loss as CO2

Fig 20: Interaction plot for SN ratios of C loss as CO2 for BS x AM






Fig 21: Interaction plot for SN ratios of C loss as CO2 for BS x C/N

Table. 4 Response Table for SN Ratios smaller the better criteria for C loss as CO2

Level Brewery

sludge

Amendment C/N ratio starting

culture

Aeration

rate

1 -30.84 -31.80 -32.69 -30.60 -31.52

2 -30.61 -29.65 -28.76 -30.85 -29.93

Delta 0.22 2.15 3.94 0.25 1.59

Rank 5 2 1 4 3

Table 5. Analysis of variance for SN ratios for C loss as CO2

Source DF Seq SS Adj SS Adj MS F P % Contribution

BS 1 0.1011 0.1011 0.1011 2.35 0.368 0.21

AM 1 9.2697 9.2697 9.2697 215.53 0.043 19.59

C/N 1 30.9825 30.9825 30.9825 720.39 0.024 65.46

SC 1 0.1250 0.1250 0.1250 2.91 0.338 0.26

AR 1 5.0776 5.0776 5.0776 118.06 0.058 10.73

BS x AM 1 1.7303 1.7303 1.7303 40.23 0.100 3.66

Residual Error 1 0.0430 0.0430 0.0430 0.09

Total 7 47.3293 100

Optimization for loss of N as NH3

To know the influence of levels of composting factors on loss of N as NH3, the response plots of

SN ratio for main effect and interactions were done for smaller the better criteria. The response

table for SN ratios is given in Table 6 for all the levels of factors without pooling. In the table,

the difference of SN ratio between the levels of factors gives Delta and shows the rank of






influencing factors. Fig 23 represents the main effect plot for SN ratios of the loss of N as NH3

and the levels of factors that gives maximum SN ratio is selected and it is A1B2C1D1E2 for the

major contributing factors. Fig 25 represents the interaction plot for SN

Fig 22: % contribution of factors in the responses

ratios between BS and C/N ratio. Since the contribution of main effect of starting culture and interaction between BS and C/N ratio is very less on reducing loss of N as NH3, these factors

were pooled. This pooling gives an error degree of freedom 2. Therefore in the subsequent

analysis they are eliminated. From Fig 24 it is clear that the factor levels for interaction between

BS and amendment is A1B2. The optimal levels of factors that can yield less N loss as NH3 is

A1B2C1E2, considering the main effects and interaction effects. The main effect plot after

pooling D is shown in Fig 26. In order to know the factor contribution and the significance of

the factors on loss of N as NH3, analysis of variance was done and the results are presented in

Table 7. From the table it is clear that the most significant factor influencing in reducing the loss

of N as NH3 is the interaction between BS and coconut pith (p ˂ 0.05). The % contribution of

factors and error is shown in the last column of Table 7 and is represented by a pie diagram as

shown in Fig 27.

Table 6: Response table for SN ratio of loss of N as NH3

Level Brewery

Sludge (BS)

Amendment C/N ratio Starting

culture

Aeration

rate

1 -18.93 -21.50 -17.88 -19.40 -22.71

2 -21.79 -19.22 -22.84 -21.32 -18.02

Delta 2.85 2.29 4.97 1.92 4.69

Rank 3 4 1 5 2






Fig 23: Main effect plot for SN ratios for NH3

Fig 24: Interaction effect plot for SN ratios for NH3 of BS x AM

Fig 25: Interaction effect plot for SN ratios for NH3 of BS x C/N






Fig 26: Main effect plot for SN ratios for N loss as NH3 after pooling SC and BS x C/N

Table 7: Analysis of variance for SN ratios after pooling SC and BS x C/N

Source

DF Seq SS Adj SS Adj MS F P % Contribution

BS 1 16.29 16.29 16.29 2.73 0.240 6.46

AM 1 10.46 10.46 10.46 1.76 0.316 4.15

C/N 1 49.36 49.36 49.36 8.29 0.102 19.58

AR 1 44.02 44.02 44.02 7.39 0.113 17.46

BS x AM 1 120.08 120.08 120.08 20.16 0.046 47.63

Residual Error 2 11.91 11.91 5.957 4.72

Total 7 252.12 100

Conclusion

Temperature, pH, C content, N content, CO2 and NH3 evolved were continuously monitored at

regular intervals till the end of composting time of all trials for replications 1 and 2. A strong

correlation exists between temperature and CO2 evolved. With time of composting, the emission

of CO2 decreased; on the other hand the emission of NH3 decreased at the later stage of

composting. The influence of the 5 factors (A, B, C, D, E) with interactions between factors (A

x B and A x C) and optimal level of the factors on C loss as CO2 and N loss as NH3 through SN

analysis were studied. Analysis of the responses showed that C/N ratio and amendment are

significant factors in reducing the loss of C as CO2. On the other hand, the interaction between

BS and amendment is more significant in reducing the loss of N as NH3. From the study, it is

also concluded that coconut pith is effective in reducing the emission of gases formed during

composting and can be used as an odour controlling agent. The optimal level of parameters for

reducing C loss as CO2 and N loss as NH3 is A2B2C2D1E2, which gives the better compost.






Fig 27: % Contribution of factors on N loss as NH3

Acknowledgement

The funding provided by the Kerala State Council for Science, Technology and Environment for

this study is gratefully acknowledged.

Reference

1. Baddi G.A., Hafidi M., Cegarra J., Alburquerque J.A., Gonza´lvez J., Gilard V., Revel J.C.,

2004, Characterization of fulvic acids by elemental and spectroscopic (FTIR and 13C-NMR)

analyses during composting of olive mill wastes plus straw, Bioresource Technology, Vol.

93, pp. 285–290.

2. Cheng C.Y, H.C. Mei, C.F. Tsao, Y.R. Liao, H.H. Huang, Y.C. Chung, 2010, Diversity of

the bacterial community in a bioreactor during ammonia gas removal, Bioresource

Technology, Vol. 101, pp. 434-437.

3. Chiumenti A, F. Da Borso, T. Rodar and R. Chiumenti, 2007, Swine manure composting by

means of experimental turning equipment, Waste Management, Vol. 27, pp. 1774-1782.

4. de Guardia A, P. Mallard, C. Teglia, A. Marin, C. Le Pape, M. Launay, J.C. Benoist, C.

Petiot, 2010, Comparison of five organic wastes regarding their behaviour during

composting: Part 2, nitrogen dynamic, Waste Management, Vol. 30, pp. 415-425.

5. Haug R.T., 1993, The practical handbook of compost engineering, Lewis Publishers,

London, pp. 1-699.






6. Hema Nalini A.V, P.R. Sreemahadevan Pillai & Y.V.K.S. Rao, April 2015, 1, Shredded

Newspaper as a Physical Conditioner for Improving Drainability of Brewery Sludge,

International Journal of Scientific & Engineering Research, Vol. 6, Issue 4, pp. 64-69.

7. Hema Nalini. A.V, P.R. Sreemahadevan Pillai & Y.V.K.S. Rao, April 2015, 2, Simulation of

Organic Fraction of Municipal Solid Waste in the Preparation of Synthetic Compost Recipe

for Lab-Scale In-Vessel Composting, International Journal of Innovative Research in

Engineering & Management, Vol. 3, Special Issue-1, pp. 165-170

8. Hema Nalini. A.V, P.R. Sreemahadevan Pillai & Y.V.K.S. Rao, July 2015, Effect of Carbon

Nitrogen ratio on Nitrogen loss in the Co- Composting of Municipal Solid Waste and

Brewery Sludge, Proceedings of the International Conference on Energy and Environment

Management, Dept. of EEE, NSSCE & IETE, Palakkad, India, pp. 1-6.

9. Hobson A., Frederickson J. and Dise N., 2005, CH4 and N2O from mechanically turned

windrow and vermicomposting systems following in-vessel pre-treatment, Waste

Management, Vol. 25, pp. 345-352.

10. IS 10158, 1982, Methods of Analysis of Solid Wastes Excluding Industrial Solid Wastes,

Bureau of Indian Standards, pp. 1-24.

11. Jiang T, F. Schuchardt G. Li, R. Guo, Y. Zhao, 2011, Effect of C/N ratio, aeration rate and

moisture content on ammonia and greenhouse gas emission during the composting, Journal

of Environmental Sciences, Vol. 10, No. 201, pp. 1754-1760.

12. Keeney D.R. and Nelson D.W., 1982, Nitrogen-inorganic forms, Methods of Soil Analysis,

Part 2, Chemical and Microbiological Properties, Soil Science Society of America,

Madison, WI, pp. 9.2-13.27.

13. Mylavarapu R., 2009, UF/IFAS Extension Soil Testing Laboratory (ESTL) Analytical

Procedures and Training Manual, Circular 1248, Soil and Water Science Department,

Florida Cooperative Extension Service, Institute of Food and Agricultural Sciences,

University of Florida, pp. 46:21-31.

14. Ranjit Roy, 1990, A primer on the Taguchi Method, Van Nostrand Reinhold, New York, pp.

1-247.

15. Robert H. L. and Joseph E.M., 1990, Design for quality – an introduction to the best of

Taguchi and western methods of statistical experimental design, Chapman & Hall

Publishers, pp. 212-213.

16. Robert K. Ham and Dimitris Komilis, 2003, A Laboratory Study to Investigate Gaseous

Emissions and Solids Decomposition During Composting of Municipal Solid Waste, EPA-

600/R-03/004, US Environmental Protection Agency, Washington, pp. 3.8 to 3.9.

17. Samy S. Sadaka, T.L. Richard, Terrance D. Loecke and Matt Liebman, 2006, Determination

of Compost Respiration Rates Using Pressure Sensors, Compost Science & Utilization, Vol.

14, No. 2, pp. 124-131

18. Sánchez A., et. al., 2015, Greenhouse Gas from Organic Waste Composting: Emissions and

Measurement, Environmental Chemistry for a Sustainable World, Springer International

Publishing, Switzerland, pp. 33-42.

19. Xueling Sun, 2006, Nitrogen Transformation in Food Waste Composting, Master’s Thesis,

University of Regina, Saskatchewan, pp. 1-179.



Documents

CARBON DIOXIDE AND AMMONIA EMISSION DURING CO … Issue... · Co-Composting of Organic Fraction of Municipal Solid Waste and Brewery Sludge Contact Us : [email protected] ; ... Where