effect of msw compost on microbiological and biochemical soil quality indicators

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Effect of MSW Compost onMicrobiological and Biochemical SoilQuality IndicatorsP. Bhattacharyyaa, K. Chakrabartib & A. Chakrabortyc

a Department of Geology and Geophysics, Indian Institute ofTechnology, Kharagpur, West Bengal, Indiab Department of Agril. Chemistry & Soil Science, Faculty ofAgriculture, Calcutta University, Calcutta, Indiac Department of Agronomy, Bidhan Chandra Krishi Viswavidyalaya,Mohanpur, West Bengal, IndiaPublished online: 23 Jul 2013.

To cite this article: P. Bhattacharyya, K. Chakrabarti & A. Chakraborty (2003) Effect of MSW Composton Microbiological and Biochemical Soil Quality Indicators, Compost Science & Utilization, 11:3,220-227, DOI: 10.1080/1065657X.2003.10702130

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220 Compost Science & Utilization Summer 2003

Compost Science & Utilization, (2003), Vol. 11, No. 3, 220-227

Effect of MSW Compost on Microbiological andBiochemical Soil Quality Indicators

P. Bhattacharyya1, K. Chakrabarti2 and A. Chakraborty3

1. Department of Geology and Geophysics, Indian Institute of Technology, Kharagpur, West Bengal, India

2. Department of Agril. Chemistry & Soil Science, Faculty of Agriculture, Calcutta University, Calcutta, India

3. Department of Agronomy, Bidhan Chandra Krishi Viswavidyalaya, Mohanpur, West Bengal, India

This laboratory incubation study was conducted to evaluate the effect of municipalsolid waste compost (MSWC) as a soil amendment on soil quality indicators, suchas microbial biomass, and their activities. The MSWC was compared against cowdung manure (CDM), a traditional organic supplement. The comparative study wascarried out in water regimes of 60% water holding capacity (WH) of soil and underwaterlogged (WL) condition. MSWC was applied to an alluvial soil (Typic Flu-vaquent) at the rates of 0, 2.5, 10, 20 and 40 and CDM at 0, 20 and 40 t/ha. Microbialbiomass-C (MBC), glucose induced soil respiration (SR), urease and acid phos-phatase activities in soil were analyzed following 15, 30, 45, 60, 90 and 120 days ofincubation. The parameters studied were significantly higher in CDM-treated thanin MSWC-treated soils. Increase in graded doses of MSWC from 2.5 to 40 t/ha sub-stantially increased the MBC, SR, urease and phosphatase activities in the soil. In60% WH regime, MBC and SR increased for the first 30 days of incubation and thendeclined. Under the WL regime, the MBC declined while SR increased from 15 daystill 120 days of incubation. Urease and phosphatase activities of soil increased for upto 60 days during incubation in 60% WH regime and then decreased. Activities ofboth the enzymes under WL regime decreased progressively during incubation.There were no negative impacts on the soil quality indicators from high applicationrates of MSWC.

Introduction

Little information is available on use of municipal solid waste compost (MSWC)under waterlogged condition, such as is encountered in rice paddies. Water loggingoften alters chemical and microbial processes that influence nutrient cycling and ac-cumulation of toxins. Reduced environment may cause more metals to go into soil so-lution, which may be toxic to microorganisms (Gianfreda and Bollag 1996) and to en-zyme activities (Pulford and Tabatabai 1988). The present paper reports the effect ofgraded doses of MSWC in comparison to the widely used cow dung manure on mi-crobial biomass carbon, glucose induced soil respiration, urease and phosphatase ac-tivities of an alluvial soil at two water regimes under laboratory conditions.

Materials and methods

An alluvial soil (Typic Fluvaquent) collected from a rice field of the AgriculturalExperiment Farm of Calcutta University located at Baruipur (22°2` N and 88°26`E),West Bengal, India was used. One kilogram (Kg) of soil was mixed thoroughly withMSWC or CDM and kept in containers for incubation at 30°C. The principal charac-teristics of soil, MSWC and CDM, are described in Table 1.

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Effect of MSW Compost on Microbiological and Biochemical Soil Quality Indicators

Compost Science & Utilization Summer 2003 221

The experiment was conducted in a factorial completely randomized design(CRD) with each treatment replicated twice. The Factor A consisted of soil applicationrates of MSWC at 0, 2.5, 10, 20, 40 and CDM 0, 20, 40 t/ha. The Factor B consisted ofperiodic intervals of incubation at 15, 30, 45, 60, 90 and 120 days. The Factor C con-sisted of two water regimes at 60% water holding capacity of soil (WH) and water-logged condition (WL). At different periods of interval, the soils were collected fromthe containers and analyzed for MBC, SR, urease and acid phosphatase activities.Physicochemical characteristics and heavy metals content of soil (total, DTPA and wa-ter extractable), MSWC and CDM were determined by the standard methods. Micro-bial biomass-C of soil was measured following the fumigation-extraction method us-ing a calibration factor of KEC = 0.38 (Joergensen 1995). Soil respiration was determinedby glucose induced CO2 evolution from soil at 22°C (Alef 1995). Urease and acid phos-phatase activities of soil were measured by the methods proposed by Tabatabai andBremner (1972) and Tabatabai and Bremner (1969) respectively. The results are ex-pressed as moisture free basis. IRRISTAT statistical package developed by BiometricsUnit, IRRI, Philippines, was used for statistical calculations.

TABLE 1Characteristics of soil, municipal solid waste compost (MSWC) and cow dung manure (CDM)

Parameters Soil MSWC CDM

pH 5.5 7.4 6.11

Ec(dS/m) 0.294 2.7 2.17

Sand(%) 25.64 40 -

Silt(%) 28.64 30 -

Clay(%) 45.22 30 -

Organic carbon(g/kg) 13.9 114.3 110

Total nitrogen(g/kg) 1.7 10.1 9.5

C/N 8.2 11.31 11.6

Mineralizable nitrogen(mg/kg) - 160 230

Water soluble carbon(mg/kg) - 542 679

Total phosphorous(mg/kg) 60 4900 4920

Available phosphorous(mg/kg) 6.2 274 352.35

Available potassium(g/kg) 0.107 2.12 2.37

CEC (cmol(p+)/kg) 19x 105y 68.4z

Carbohydrate content (µg glucose/100g) - 600 1300

Zn (mg/kg) Total 50 691 170

DTPA extractable 16 213 4

Water extractable 0.05 7 B.D.L

Cu (mg/kg) Total 21 149 10

DTPA extractable 4 74 0.25


Pb (mg/kg) Total 22 319 28.99

DTPA extractable 3 157 0.12


Cd (mg/kg) Total 0.75 3 B.D.L

DTPA extractable B.D.L B.D.L B.D.L

Water extractable B.D.L B.D.L B.D.L

x Ammonium acetate method; B.D.L = Below detectable limit; y and z Barium acetate method (ash free basis)

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P. Bhattacharyya, K. Chakrabarti and A. Chakraborty


Results and Discussion

Microbial Biomass-C

Fumigation-extraction method (Joergensen 1995) for microbial biomass carbon de-termination was followed. This method is suitable for acidic soils and those recentlyamended with organic matter, such as the condition of this experiment. The soils withorganic input (i.e., CDM and MSWC) treatments showed significantly higher levels ofMBC than did those without any treatment (Table 2). CDM-treated soils showed sig-nificantly higher levels of MBC than did the MSWC-treated samples. There was also acorresponding significant increase in MBC of soil with each graded dose of 2.5 to 40t/ha. The trend of periodic variation in soil MBC with water regimes at WH and WLvaried, except the no input treatment, wherein a continuous decrease was obtainedfrom 15 days of incubation. During the incubation in WH regime, the MBC in soil in-creased steadily up to 30 days, where after it declined steadily to its lowest level byday 120. In contrast, under the WL regime, the decrease in the peak values was ob-served from 15 days onwards. The mean value of MBC in soil was statistically signif-icant in WH than WL regime. Significant variation between the mean MBC values atdifferent periods was also observed (P < 0.05). The highest and lowest values were at15 and 120 days of incubation respectively.

TABLE 2.Dynamics of microbial biomass-C in soil with or without treatment at two water regimes

Incubation Period (days)Water 15 30 45 60 90 120 Mean

Treatment Regime (µg/g soil)

No input (T1) WHy 242 182 172 147 136 132 168.5WL 194 154 148 134 118 108 142.7

2.5 t/ha MSWCx (T2) WH 286 337 309 248 213 191 264.0WL 227 192 161 146 126 114 161.0

10 t/ha MSWC (T3) WH 339 383 339 291 257 243 308.7WL 271 202 172 156 136 122 176.5

20 t/ha MSWC (T4) WH 381 416 372 322 280 274 340.8WL 285 212 189 168 146 127 187.8

40 t/ha MSWC (T5) WH 425 456 413 367 315 298 379.0WL 315 255 215 185 165 145 213.3

20 t/ha CDM (T6) WH 415 480 446 400 354 309 400.7WL 302 234 210 179 153 135 202.2

40t/ha CDM (T7) WH 455 525 485 455 405 365 448.3WL 325 285 255 225 185 155 238.3

Mean 318.7 308.1 277.6 244.5 213.5 194.1Mean treatment T1 T2 T3 T4 T5 T6 T7

155.3 213.7 242.8 264.4 296.2 301.4 343.3Mean water regime WH WL

330.3 188.8F-LSD Treatment (T) 4.21(p=0.05) Period (P) 3.89

Water regime (W) 2.25

T x P 10.3

T x W 5.95

P x W 5.95

T x Px W 14.57

xMSWC = Municipal solid waste compost, CDM = Cowdung manure yWH = 60% water holding capacity, WL= Waterlogged condition

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Incorporation of CDM and MSWC, both organic supplements, increased the MBCin soil. Pascual et al. (1997) stated that incorporation of organic materials includingMSWC usually increases the soil MBC. Higher MBC in the CDM enriched soils overthe MSWC-treated soils testifies to the qualitative difference between the two materi-als (Sakamoto and Oba 1991). Water soluble carbon, carbohydrate and mineralizableN were higher in CDM (Table 1). These acted as energy sources for the microorgan-isms in soil, hence contributing to the increase in biomass. Manifestation of higherMBC in soil with increasing doses of CDM or MSWC was due to application of high-er amounts of carbon substrate in soil (Jenkinson and Ladd 1981). Nutrients in soil areessential for microbial proliferation. However, shortage of nutrients in no input soilsat both WH and WL regimes created a periodic decreasing trend of MBC. In additionto nutrient shortage, microorganisms in WL regime had to face oxygen depletion stressand other detrimental influences (Ponnamperuma 1972). This caused further reduc-tion in soil MBC. Under waterlogged condition, soil environment can be virtually dom-inated by the anaerobic or facultative microorganisms that usually have minimal cellyield (Tate 2000).

Gradual increase followed by decrease in soil MBC, treated with CDM or MSWC atWH regime was also observed by Pascual et al. (1997). The gradual increase in MBC upto 30 days may have been related to the availability of biogenic materials for biomassstimulation (Jenkinson and Ladd 1981). Another reason may be the incorporation of ex-ogenous microorganisms (Perucci 1992). Decrease in soil MBC after 30 days of incuba-tion can be associated to the nutrients shortage or “protective capacity” of soil for bio-mass (Sparling 1985). Biomass, generated in excess of that protective capacity isautomatically killed or lysed resulting in lower biomass. At 120 days of incubation or-ganic matter treated soils had higher MBC than did the soil sample with no input. Thiscould be the consequence of partial protection of biomass by the humus substances inCDM or MSWC (Pascual et al. 1997). The soil MBC decreased from 15 days of incubationunder WL condition irrespective of treatments. This may have originated largely fromthe anaerobic bacteria with oxygen depletion. Nutrient shortage was probably not a lim-iting factor as the anaerobic bacteria are less efficient in carbon assimilation (Alexander1977). Higher MBC levels, at all stages of incubation, in soil enriched with MSWC thanin soils with no input indicate an improvement in the microbiological component of soil.Apparently there was no indication of interference by the heavy metals in MSWC.

Soil Respiration

Measurement of SR is a dependable procedure for the assay of general meta-bolic activity of soil microorganisms (Nannipieri et al. 1990). SR, induced by glucoseaddition to moist soil, was measured at 22°C for 5 hours. Thus the measurement ofSR for short incubation time reflects the metabolic activity of the original and notthe regenerated biomass. Notably, soils enriched with CDM or MSWC, at all thedoses, showed increased SR as compared to the no input treatment (Table 3). Soilapplication of CDM significantly increased SR than did MSWC, as also the WLregime compared to WH. The periodic variation of SR was not similar in WL andWH regimes, excepting the no input treatment. During 30 days of incubation the SRvalues reached to a peak and subsequently decreased to the lowest at 120 days inWH regime. But with the no input treatment only, under WH regime, SR decreasedafter 15 days up to 120 days of incubation. There was statistically significant varia-tion between the periods of incubation. The highest SR was obtained at 120 daysand the lowest at 15 days of incubation .

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Incorporation of carbon substrate through CDM or MSWC instantaneously in-creased SR. High adenylate charge, maintained by the organisms, partly illustrate theirability to respond readily to exogenously added substrates. The growth and activityare concomitant to the decline in substrate availability (Table 3). The small amount ofsubstrate is used for maintenance (Sparling 1985). The same phenomenon was ob-served in WH regime. But gradual increasing trend of SR under WL regime in all thetreatments probably reflected the carbon assimilating potential of the microorganisms(Alexander 1977). Under WL situation, the anaerobic bacteria dominated the soil sys-tems. These are poor assimilators of organic carbon, evolving more waste products likeCO2 and other low molecular weight organic compounds. Higher SR in CDM orMSWC than no input treatment pertains to the higher MBC in the supplemented soils.

Soil Enzyme Activities

Significantly increased urease and acid phosphatase activities were observed insoil samples supplemented with CDM or MSWC (Tables 4 & 5). The two enzymes as-sayed showed positive correlation with the doses of the organic supplement used, withthe CDM-supplemented soil samples showing higher activities than the MSWC-sup-plemented samples. Enzyme activities, under WH regime, increased up to 60 dayswith all the treatments and then declined. At 120 days of incubation urease activity of



TABLE 3.Dynamics of respiration of soil with or without treatment at two water regimes


Treatment Regime (µg CO2/10 g soil/h at 22°C)

No input (T1) WHY 38 30 26 20 16 16 24.3WL 32 45 60 77 83 88 64.2

2.5 t/ha MSWCX (T2) WH 60 80 61 41 32 31 50.8WL 38 59 67 95 102 116 79.5

10 t/ha MSWC (T3) WH 75 90 78 58 45 42 64.7WL 42 78 92 122 143 178 109.2

20 t/ha MSWC (T4) WH 81 95 89 64 54 52 72.5WL 47 93 147 174 183 216 143.3

40 t/ha MSWC (T5) WH 91 105 95 74 63 59 81.2WL 52 109 158 191 198 223 155.2

20 t/ha CDM (T6) WH 90 112 106 84 75 73 90.0WL 53 114 176 254 282 291 195.0

40t/ha CDM (T7) WH 108 118 111 89 81 76 97.2WL 61 121 189 267 297 309 207.3

Mean 62 89.2 103.9 115.0 118.1 126.4Mean treatment T1 T2 T3 T4 T5 T6 T7



Water regime (W) 0.63TXP 2.87TXW 1.66PXW 1.54

TXPXW 4.06


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soils treated with MSWC recorded either significantly lower values at lower applica-tion rates or similar values at higher rates during 15 days of incubation than that of noinput treatment. However, CDM treated soils maintained higher urease activity at 120days than the corresponding values at 15 days of incubation. In contrast, at 120 daysof incubation, phosphatase activity of soils treated with CDM or MSWC at all appli-cation rates maintained significantly higher values than at 15 days . Under WL regimeboth the enzyme activities progressively declined with all the treatments attaining thelowest at 120 days of incubation. Mean periodic variation of urease and acid phos-phatase activities gradually increased up to 60 days and then declined. Both the en-zyme activities were significantly higher in WH than WL regime.

The source of enzymes in soil is not definitely known, but presumed to originate frommicroorganisms, plant roots and soil animals (Tabatabai 1982). Since the soil samples inthis study were devoid of extraneous plant and animal materials , it is safe to assume thatthe enzyme activities were elaborated by the microorganisms (Gianfreda and Bollag 1996).Urease and phosphates activities, which are also sensitive to heavy metals (Tyler 1981), areimportant measures of microbial activity in the cycling of nitrogen and phosphorus in soil.

Soil contains both acid and alkaline phosphatases. Since the soil in this study wasacidic, activity of acid phosphatase was measured. That the addition of CDM or MSWCincreased the enzyme activities in soil are in agreement with Giusquiani et al. (1994) andPerucci (1990). Such increases in enzyme activities were mediated by the increases in

TABLE 4.Dynamics of urease activity in soil with or without treatment at two water regimes


Treatment Regime (µg urea hydrolyzed/g soil/h at 37°C)

No input (T1) WHY 25 31 35 39 26 16 28.7WL 18 14 12 9 8 8 11.5

2.5 t/ha MSWCX (T2) WH 29 36 40 49 36 26 36.0WL 22 17 16 12 10.5 10 14.6

10 t/ha MSWC (T3) WH 43 56 67 75 62 40 57.2WL 26 21 20 15 12.5 12 17.8

20 t/ha MSWC (T4) WH 54 63 80 93 75 52 69.5WL 30 25 23 17 12 12 19.8

40 t/ha MSWC (T5) WH 62 71 88 98 81 61 76.8WL 36 31 27 22 17 17 25.0

20 t/ha CDM (T6) WH 59 71 93 104 85 62 79.0WL 34 28 25 20 16 14 22.8

40t/ha CDM (T7) WH 68 87 103 109 91 73 88.5WL 39 35 31 25 21 21 28.7




Water regime (W) 0.36TXP 1.67TXW 0.96PXW 0.89

TXPXW 2.36


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microbial biomass and hence may be considered a direct contribution of organic inputs(Martens et al. 1992). Elevated levels of enzyme activities due to more organic inputscan also be similarly explained. The periodic variation of enzyme activities of soils atWH regime did not follow the trend of MBC and SR that were found to increase up to30 days of incubation and subsequently declined. The increased enzyme activities ofsoil up to 60 days, even after the decrease in MBC, seemed to be related to active en-zymes within dead cells, associated cell fragments and activity of living cells (Skujins1976). The fall of urease activity and the maintenance of higher phosphatase activity ofsoil at 120 days of incubation corresponding to the values at 15 days project the differ-ential behavior of “protective capacity” of soil due to these two enzymes. It may havealso be the result of continued production of phosphatases by the existing microorgan-isms, while the reverse phenomenon occurred in the case of urease. Lower enzyme ac-tivity in WL, as compared to the WH, regime agrees with the earlier observation of Pul-ford and Tabatabai (1988). The decrease in enzyme activities in the soil with or withouttreatments probably resulted from the increase in reduced metals in WL soils.

Conclusion

The major objection in the use of MSWC as soil supplement has been the possibilityof the detrimental influence of heavy metals content on soil quality indicators like MBC,

TABLE 5.Dynamics of acid phosphatase activity in soil with or without treatment at two water regimes


Treatment Regime (µg pnp released/g soil/h at 37°C)

No input (T1) WHY 518 564 596 645 622 594 589.8 WL 274 205 186 154 146 136 183.5

2.5 t/ha MSWCX (T2) WH 530 591 645 700 634 625 620.8WL 292 222 200 170 157 150 198.5

10 t/ha MSWC (T3) WH 562 667 682 725 656 647 656.3WL 313 242 226 193 181 170 220.8

20 t/ha MSWC (T4) WH 604 685 708 754 706 685 690.3WL 331 258 238 226 222 203 246.3

40 t/ha MSWC (T5) WH 625 715 735 785 745 715 720.0WL 355 285 255 244 233 223 265.8

20 t/ha CDM (T6) WH 644 699 718 780 756 720 719.5WL 374 308 256 241 230 217 271.0

40t/ha CDM (T7) WH 685 735 765 810 775 735 750.8WL 405 345 285 262 242 234 295.3


365 387.5 408.5 444 469 468.5 484Mean water regime WH WL


Water regime (W) 1.66TxP 7.6TxW 4.39PxW 4.06

TxPxW 10.75

xMSWC = Municipal solid waste compost, CDM = Cowdung manure; yWH = 60% water holding capacity,WL = Waterlogged condition

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SR and enzyme activities. In this study, we have demonstrated that the application ofMSWC, even at a rate as high as 40 t/ha, does not negatively impact the soil quality pa-rameters. We have indeed shown that the soil quality is enhanced upon the applicationof MSWC as an ameliorating agent. We propose that under such conditions where tra-ditional organic supplements are scarce, MSWC can be safely used. However, long-termmonitoring of changes in soil quality parameters under field condition is necessary.

Acknowledgements

We thank West Bengal Pollution Control Board and Nodal Research Center, Cal-cutta, India for financial and administrative assistance.

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effect of msw compost on microbiological and biochemical soil quality indicators

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