Effect of Heavy Metals on Earthworm Activities During Vermicomposting of Municipal Solid Waste

Written By: Sam Savage

Published Date: February 24, 2008 Last Edited: February 24, 2008

By Kumar, Sunil Sharma, Vishal; Bhoyar, R V; Bhattacharyya, J K; Chakrabarti, Tapan

ABSTRACT: The effect of heavy metals on the activities of earthworm species Eudrillus eugineae was studied during vermicomposting of municipal solid waste (MSW) spiked with heavy metals. The activities of earthworms, in terms of growth and biomass production and number of cocoons produced, were monitored periodically, and the concentration of heavy metals in earthworms and substrates was determined at definite intervals. Laboratory- scale experiments were performed by mixing individual heavy metals in MSW. Copper, cadmium, chromium, lead, and zinc were selected for the study. The study concludes that heavy metals tend to accumulate in the body of earthworms; hence, the inherent concentration of heavy metals in the substrate before vermicomposting must be considered in view of composting of MSW and its application to soil. It was observed that copper and cadmium were toxic for the worms at 1.5 and 0.1 g/kg of the waste, respectively. The studies also suggest that earthworms are susceptible to the free form of heavy metals. Cadmium is the most toxic metal, followed by copper. Based on the investigation and observation, it was also found that earthworms should be separated from castings before the use of castings in soil amendments. Water Environ. Res., 80, 154 (2008).

KEYWORDS: earthworms, cocoons, contaminants, absorption, castings, biomass.

doi:10.2175/106143007X220824

Introduction

Rapid urbanization and a growing number of industries coupled with increasing population have resulted in a quantum increase of municipal solid waste (MSW) generation, and this production is expected to increase in subsequent years. Although large numbers of technologies are available for managing MSW, their applications are limited because of their high costs, infrastructure, and energy requirements. Options such as landfilling have become limited, as a result of the paucity of land for disposal, and incineration is not publicly acceptable or feasible or is very expensive, as a result of the low calorific value of MSW generated in India (NEERI Report, 1996).

Management of MSW in an environmentally compatible manner adopting principles of economy, aesthetics, energy, and conservation is needed. Biotechnological treatments, such as composting and vermicomposting, have emerged as feasible options for converting MSW into nutrient-rich compost or organic biofertilizer.

Vermicomposting is a process in which earthworms play a major role with microbes in the conversion of organic solid waste into more stabilized and nutrient-rich compost that is rich in major and micronutrients, such as nitrogen, phosphorus, potassium, magnesium, sodium, and zinc (Benitez et al., 2002). Vermicomposting seems to provide a good quality end product without odor and is also aesthetic in appearance. Moreover, it does not require skilled personnel and mechanization. The MSW contains an appreciable amount of nutrients that can provide ample nutrition if applied as a manure. The use of these materials is possible only when they are converted to harmless substrates, such as by a bioprocessing approach (Beyer et al., 1982).

However, the process is influenced by various physicochemical factors, among which, the toxic heavy metals are of much concern. A review of research on the use of earthworms in MSW processing and application of vermicasts in land has raised con- , cerns over the concentration of heavy metals in MSW. These metals may adversely affect earthworm activities and the overall vermicomposting process. Earthworms are known to accumulate heavy metals (Amoji et al., 2000; Ash and Lee, .1980; Hopkin, 1989). Vermicompost from solid waste invariably will contain these elements, although at low concentrations. Heavy metals selected for this study are copper, cadmium, chromium, lead, and zinc.

Metals enter the MSW stream from a variety of sources. Industrial discharges, pharmaceutical waste, insecticides, batteries, motor oils, paint chips, consumer electronics and electricals, house dust, lead foils, vehicular emissions, and other allied activities introduce metals to the solid waste stream. Heavy metals have relevance in the following two ways:

(1) They may be lethal to worms, thereby affecting vermiconversion; and

(2) They may enter the food chain through the application of MSW or MSW compost to soil.

In small amounts, trace elements, such as copper, zinc, and chromium, are essential for the growth of plants or animals. Cadmium, lead, and chromium are of prime concern as contaminants because of their potential to harm soil organisms, animals, and humans, and these should receive close scrutiny in relation to the application of MSW to agricultural land and to the overall vermicomposting process (Atiyeh et al., 2000; Collins and Stotzky, 1989). Information on vermicomposting of MSW, in terms of heavy metal concentration and its effect on earthworms, are scanty.

The present study envisages primarily how these heavy metals affect earthworm activities, in terms of their growth, reproduction, and cocoon production, and the overall process of vermicomposting. In the present study, the valence states of heavy metals in the waste during composting are not considered.

Experimental Studies

Laboratory-scale experiments were conducted, in triplicate, to determine the effect of heavy metals on the activities of earthworms, in terms of their growth, population, and cocoon formation and the effects on the process of vermicomposting. Municipal solid waste containing an inherent concentration of heavy metals was used as a control during various studies. To avoid the influence of decomposition products, such as volatile fatty acids and gaseous ammonia, and the effects of increased temperature in the waste mass, the waste was allowed to predecompose for approximately 15 days (Amoji et al., 2000). The predecomposed MSW (approximately 2 kg dry wt.) was placed in earthen pots and used as a substrate for conducting experiments. The experiments were conducted for 90 days.

Materials. All of the chemicals and reagents used in the study were of analytical grade. The Merck inductively coupled plasma (ICP) multi-element standard solution IV (23 elements) (Merck KgaA, 64271, Darmstadt, Germany) was used as a standard for plotting calibration curves and for determination of the concentration of heavy metals by inductively coupled plasma atomic emission spectrometry (ICP-AES). The ICP-AES (Perkin-Elmer, Wellesley, Massachusetts) was used to analyze heavy metals in earthworms and substrate samples (Beyer et al., 1982).

The metals, such as copper, cadmium, chromium, lead, and zinc, in the form of metallic salts, were used in the study. The MSW was spiked with these metals in the concentration range 0.5 to 3.5 g/kg of the waste. Similarly, a 10-mg/L solution of individual metals was prepared in double-distilled water to assess the effect of the free form of metals.

The MSW used as a substrate in the experimental studies was obtained from Municipal Corporation, Nagpur, India, which is a second capital of Maharashtra State, with an approximate population of 2.5 million. The physical composition of the waste is presented in Table 1.

Earthworms of the species Eudrillus eugineae were obtained from Go-vigyan Kendra, Nagpur, India. Cow dung, known to be one of the best natural feeds for earthworms, was used as a medium for culturing earthworms.

A microwave digestion system (Ethos 900, Milestone, Italy) was used for digesting earthworms and substrate samples (Booth et al., 2001).

Methods. The laboratory-scale investigations were carried out in the following three parts:

(1) Part I: Effect of heavy metals on earthworms in distilled water,

(2) Part II: Effect of inherent concentration of heavy metals in MSW, and

(3) Part III: Vermicomposting of MSW spiked with individual heavy metals.

The toxic effects of heavy metals vary, depending on the state of heavy metals (i.e., free forms), concentration, reactivity, complex formation, and stability (Nieboer and Fletcher, 1996). Studies were conducted to determine the effect of the free or organically bound form of heavy metals.

Effects of Heavy Metals in Distilled Water. To assess the effect of the free form of heavy metals, the individual metal solution of 10 mg/L copper, cadmium, chromium, lead, and zinc were prepared in double-distilled water. Double-distilled water was taken as a control for the study. Five adult earthworms were introduced to each metal solution, and preparations were made to monitor their activities. Similarly, various permutation combinations of metal solutions were prepared by mixing 10 mg/L aqueous solutions, and earthworms (5 per 500 mL) were added to the mixed metal solution. Table 2 presents finding of the individual and mixed heavy metals. The heavy metal concentration in the control MSW is presented in Table 3.

Vermicomposting of Municipal Solid Waste with an Inherent Concentration of Heavy Metals. The study was conducted to provide a larger and more comprehensive examination of vermicomposting of MSW, with respect to the concentration of heavy metals. The laboratory- scale studies (in triplicate) were performed in earthen pots. Adult earthworms (10 per kg of waste) were added to each pot. The temperature was maintained between 27 and 29[degrees]C. Water was maintained between 45 and 50 % substrate by spraying water at a regular interval during the studies. The experimental pots were aerated by turning at definite intervals. Earthworms and substrate samples were obtained periodically and analyzed to determine die concentration and status of heavy metals. Similarly, the growth of earthworms, in terms of their population, reproduction, and cocoon formation, was also assessed periodically (i.e., in 30,60, and 90 days). The findings are discussed in the Results and Discussion section.

Vermicomposting of Municipal Solid Waste Spiked with Individual Heavy Metals. The toxicity of heavy metals to organisms depends on the valence state of the metals, contact time with the organism, and their concentration (Holm et al., 1995). The laboratory-scale experiments were performed in triplicate in earthen pots. Copper, cadmium, chromium, lead, and zinc were selected for the study. For every individual metal, experiments were conducted separately using different concentrations of heavy metals (0.5 to 3.5 g/kg of waste). Simultaneously, experiments were conducted with MSW having an inherent concentration of heavy metals. Predecomposed MSW was mixed with individual heavy metals of the above-stated different concentrations. The metals were uniformly mixed; each earthen pot was labeled accordingly. Adult earthworms (10 per kg of waste) were added at the start of the experiment. The activities of the earthworms were monitored, in terms of their growth in numbers, biomass production, and cocoon production. Samples of earthworms and substrates were collected periodically and analyzed. The changes in chemical composition of the substrate, in terms of metal concentration (initial and final), were also determined. The pots were watered periodically, and the contents were mixed for aeration. The temperature was controlled to remain between 27 and 29[degrees]C. During the experiment, no new substrate was added. The results are depicted in Tables 4 to 7 and Figures 1 to 3.

Sampling and Analysis. The concentrations of heavy metals were determined in earthworms and substrates samples and castings. Earthworms were lyopholized at – 30[degrees]C, dried at 100 +- 5[degrees]C, weighed, and digested with concentrated nitric acid (analytical-grade) in a microwave digestion system (Ethos 900), as per the methodology described by Knight et al. (1998) and Marquenie (1988). Similarly, substrate samples (0.5 g) were weighed, mixed with 10 mL concentrated nitric acid (analyticalgrade), and digested by a microwave digestion system. A preset microwave program of 15 minutes was adjusted in three steps, as follows: 5 minutes at 500 W, followed by 7 minutes at 400 W, followed by 3 minutes at 250 W. The samples were filtered and analyzed for heavy metals. Estimation of heavy metals was carried out as described by Marinussen et al. (1997). Extraction of organically bound and exchangeable forms of heavy metals in substrates was carried out as per the method described by Emmerich et al. (1982).

The portions (both for the organically bound and exchangeable form of metal) were filtered by a Millipore filter assembly (Milhpore, Bedford, Massachusetts) with glass microfiber filter paper (pore size of 0.45 micron), and the total volume was increased to 100 mL using 1 M nitric acid.

The concentrations of total heavy metal content in earthworms, substrates, and castings, and organically and exchangeable forms in substrates were measured by ICP-AES, as per the methodology described by Knight et al. (1998).

Results and Discussion

Solubility is an important determinant in metal toxicity (Nieboer and Fletcher, 1996). The extent of toxic agent that the animal body tolerates determines the reactivity. To obtain information on the effect of the free form of heavy metals on earthworms, the aqueous extract of metals was tested separately and in combination.

Copper constitutes an essential trace metal and hence was selected for investigation. Cadmium was selected because of its relatively higher toxicity, and chromium was selected because its toxicity depends on its oxidation state-Cr(IfI) or Cr(VI) (Kimbrough, 1999). Lead was chosen for study because it is deposited commonly from vehicular emission, lead foils, flue gases, and other sources, and zinc was selected for its high ambient concentration in MSW.

The result of the free form of heavy metals in the aqueous phase (Table 2) indicates a pronounced synergetic effect of the combination of metals in solution relative to the use of an individual metal in solution. The concentration of heavy metals was more in the integument than in the alimentary canal, suggesting integument absorption of metals in free form. The worms were dissected to separate the alimentary canal and integument. Copper and cadmium were highly toxic for worms, as the worms died within a few hours after introduction of the metals. Within hours of the introduction of free metals, the movements of earthworms became abnormal and later slowed down. In copper and cadmium solution, their clitella became swelled, and several ruptures in the body were seen also. It was observed that combinations of metals produced more pronounced toxicity than the individual metals (Olaniya and Bhide, 1990; Oste et al., 2001). The earthworms were presumed dead when they did not respond to external stimuli by touching or pricking. Earthworm mortality in aqueous metals solutions may result from ingestion and absorption through integument. Integumentary uptake of dissolved organics was reported by Sylvia and Arme (1982).

The concentrations of heavy metals inherently present in MSW obtained from Municipal Corporation, Nagpur, India, did not influence the activity of earthworms. Appreciable growth in the earthworm population was observed; the earthworms increased from an initial 20 to 400 in 90 days, and the number of cocoons was also observed to be in the hundreds. Analysis of the samples determined that the metals are more in organically bound forms. After 3 months, the earthworms had turned the odorous and unaesthetic MSW into fine granular odorless and soft castings.

During aerobic degradation of the waste mass, the pH is in the alkaline range; therefore, solubilization of heavy metals is negligible. Under such conditions, the effect on the activity of the earthworm is a function of dose response (i.e., intake of feed substrate and concentration of heavy metals in it [Loehr et al., 1985; Raymond et al., 1985]). Hence, experiments were conducted to obtain a comprehensive feature of the vermicomposting process under different concentrations of heavy metals in MSW.

Studies were carried out by fortifying MSW with individual metals (copper, cadmium, chromium, lead, and zinc). Cadmium was the most toxic metal, followed by copper for earthworms, and hampered the overall vermicomposting process. Composting in the presence of cadmium at concentrations in excess of 0.1 g/kg was unfavorable for earthworm and vermicomposting, whereas copper was toxic at 1.5 g/ kg. However, at the concentrations provided, other metals, such as chromium, lead, and zinc did not affect the activities of earthworms; considerable growth, in terms of population and cocoon formation, was observed in experiments with these metals up to 2.5g/ kg. However, from 2.5 g/kg upwards, their concentration in waste became unfavorable for earthworms and the overall vermicomposting process. Tables 4 and 8 and Figure 1 show the population of earthworms and production of cocoons during vermicomposting of MSW mixed with copper, chromium, lead, and zinc for 90 days. The studies with these metals are discussed below.

Studies with Copper. Copper is an essential trace metal for growth. Copper at 0.5 g/kg of waste was favorable for earthworms, as the percent increases in their population were 155, 610, and 800% for 30, 60, and 90 days, respectively. As the concentration of copper increased from 0.5 g/kg of waste, the population of earthworms and cocoons decreased and significantly decreased at the 1.5-g/kg concentration. Copper at 2.0 g/kg of waste became toxic for earthworms, as they were found dead with 15 days of the experiment. As the concentration of copper increased in the waste, the metal accumulated more in the earthworms (Figure 2).

Studies with Cadmium. Cadmium is well-known for its toxicity in organisms (Pearson et al., 2000). Cadmium at concentrations exceeding 0.1 g/kg of waste was lethal for earthworms, as they died within 1 week. The MSW spiked with cadmium at 0.1, 0.3, and 0.5 g/ kg of waste indicated that worms could tolerate cadmium concentrations up to 0.1 g/kg in the waste (Table 8).

Studies with Chromium, Lead, and Zinc The activities of earthworms were normal with Cr(III) from 0.5 to 2.5 g/kg of waste. The percent increases in their population were 295,500, and 1000% for 30, 60, and 90 days, respectively. The concentration of chromium was higher in castings than in earthworms. Chromium at 2.5 g/kg upwards was unfavorable for vermicomposting, as the population of earthworms decreased. Similarly, percent increases of 5, 80, and 355% for 30, 60, and 90 days, respectively, in the earthworm population occurred with lead concentrations between 0.5 and 2.0 g/ kg wastes. Lead at 2.5 to 3.5 g/kg of waste became unfavorable for earthworms. Zinc also favored the process, until 0.5 to 2.5 mg/kg of the waste, as the percent increase in earthworm population was found to be 145, 525, and 1375% for 30, 60, and 90 days, respectively; however, from 2.5 g/kg upwards, zinc also showed a pattern of marginal decrease in the population of worms, as reported by Spurgeon et al. (2000).

Tables 6 and 7 summarize the data on accumulation of heavy metals in earthworms and castings during 90 days of vermicomposting. It has been observed that heavy metals, such as copper and zinc, are accumulated more in earthworms than in castings, whereas lead and chromium accumulated more in castings, as reported by Rao and Rao (2001). Integument absorption of metals was more than absorption by the alimentary canal. Figures 2 and 3 present findings for the accumulation of heavy metals in earthworms and castings. Medium Difference and Bioconcentration Factor. When earthworms cultured in medium with a high concentration of heavy metals were transferred to a medium having comparatively lower heavy metals concentration (i.e., soil), the earthworms tended to release heavy metals from their body into the surrounding medium in which they are transferred, which can be concluded from Table 9.

The bioconcentration factor was calculated for copper, chromium, lead, and zinc, as per David and Hopkin (1996). The bioconcentration factor for copper, chromium, lead, and zinc was observed to range from 0.57 to 0.92, 0.25 to 1.49, 0.11 to 0.55, and 0.84 to 1.47, respectively.

Conclusions

After comparing the data on earthworm population and cocoon formation, it is concluded that cadmium was the most toxic metal and hampered the process, even at 0.1 g/kg of waste. Copper up to a concentration of 1.5 g/kg of waste was favorable for earthworm populations and thereafter became unfavorable. Similarly, the activities of earthworms, such as growth, reproduction, and cocoon formation, were normal for chromium, zinc, and lead at concentrations between 0.5 and 2.5 g/kg of waste. However, from 2.5 g/kg upwards, their concentration in waste also became unfavorable for vermicomposting. Vermicomposting with lead at all concentrations showed an increase in population growth and cocoon formation, though at a reduced rate compared with chromium and zinc.

Credits

This manuscript has been prepared based on the findings of the project sponsored by the Department of Biotechnology, Government of India, New Delhi. The authors are thankful to the advisor and director of the Department of Biotechnology, Government of India, for their guidance and support in completing the project activities. The authors are very thankful to Sukumar Devotta, National Environmental Engineering Research Institute (Nagpur, India), for permission to release the manuscript.

Submitted for publication September 2, 2006; revised manuscript submitted June 14,2007; accepted for publication July 16, 2007.

The deadline to submit Discussions of this paper is May 15, 2008.

References

Amoji, S. D.; Pulkeshi, M. B.; Shagoti, U. M.; Biradar, V. A. (2000) Influence of Seasonal Environmental Factors on Growth and Reproduction of the Epigeic Earthworm Eisenia Foetida. J. Environ. Biol, 21, 59-63.

Ash, C. P. J.; Lee, D. L. (1980) Lead, Cadmium, Copper and Iron in Earthworms from Roadside. Environ. Pollut., 22, 59-67.

Atiyeh, R. M.; Edwards, C. A.; Subler, S.; Metzger, J. D. (2000) Earthworm Processed Organic Wastes as Components of Horticultural Potting Media for Growing Marigold and Vegetable seedlings. Compost Sci. Util, 8, 215-223.

Benitez, E.; Sainz, H.; Melgar, R; Nogales, R. (2002) Vermicomposting of Lignocellulosic Waste for Olive oil Industries: A Pilot Scale Study. Waste Manage. Res., 20, 134-142.

Beyer, W. N.; Chaney, R. L.; Mulhem, B. M. (1982) Heavy Metal Concentrations in Earthworms from Soil Amended with Sewage Sludge. J Environ. Qual, 11, 381-385.

Booth, L. H.; Hodge, S.; Halloran, K. O. (2001) Use of Biomarkers in Earthworms to Detect Use and Abuse of Field Application of Amended Organophosphate Pesticide. Environ. Contant. Toxicol, 67, 633-640.

Collins, Y. E.; Stotzky, G. (1989) Factors Affecting the Toxicity of Heavy Metals to Microbes. In Metal Ions and Bacteria, Beveridge, T. J., Doyle, R. J. (Eds.); Wiley Interscience: New York, 31-90.

David, S. J.; Hopkin, P. S. (1996) Risk Assessment of the Threat of Secondary Poisoning by Metals to Predators of Earthworms in the Vicinity of a Primary Smelting Works. Sci. Total Environ., 187, 167- 183.

Emmerich, W. E.; Lund, L. J.; Page, A. L; Chang, A. C. (1982) Solid Phase Forms of Heavy Metals in Sewage Sludge-Treated Soil. J. Environ. Qual, 11 (2), 178-181.

Holm, P. E.; Christensen, T. H.; Tjell, I. C; McGrath, S. P. (1995) Speciation of Cadmium and Zinc with Application to Soil Solution. J. Environ. Qual, 24, 183-190.

Hopkin, S. P. (1989) Ecophysiology of Metals in Terrestrial Invertebrates; Elsevier Applied Science: London.

Kimbrough, D. E. (1999) A Critical Assessment of Chromium in the Environment. Crit. Rev. Environ. Sci. Technol, 29 (1), 1-46.

Knight, P. B.; Chaudri, A. M.; McGrath, S. P.; Giller, K. E. (1998) Determination of Chemical Availability of Cadmium and Zinc in Soils Using Inert Soil Moisture Samplers. Environ. Pollut., 99, 293- 298.

Loehr, C. R.; Nenhauser, E. F.; Malecki, M. R. (1985) Factors Affecting the Vermistabilization Process. Water Res., 19, 1311- 1317.

Marinussen, M. P.; Sjoerd, E. A.; Vander Zee, T. M.; Frans, A. M. (1997) Cu Accumulation in Earthworm Dendrobaena Veneta in a Heavy Metal (Cu, Pb, Zn) Contaminated Site Compared to Cu Accumulation in Laboratory Experiments. Environ. Pollut., 96 (2), 227-233.

Marquenie, I. M. (1988) A Method to Assess Potential Bioavailability of Contaminants. Earthworms Environ. Waste Manage., 367-365.

NEERI Report (1996) Strategy Paper on Solid Waste Management in India, Final Report Appendix II; National Environmental Engineering Research Institute: Mumbai, India, 38-43.

Nieboer, E.; Fletcher, G. G. (1996) Determinant of Reactivity in Metal Toxicity. In Toxicology of Metals, Chang, L. W. Qsd.); CRC Press: Boca Raton, Florida.

Olaniya, M. S.; Bhide, A. D. (1990) Heavy Metals Status in Some of Indian City Refuse. Paper presented at the International Conference on Heavy Metals in Indian Environment, Aligarh, India, Jan. 8-10; IAEM: India, 59-70.

Oste, L. A.; Dolfing, J.; Ma, C-W; Lexmond, T. M. (2001) Cadmium Uptake by Earthworms as Related to the Availability in the Soil and the Intestine. Environ. Toxicol Chem., 20 (8), 1785-1791.

Pearson, S. M.; Maenpaa, K.; Pierzynski, G. M.; Lydy, M. J. (2000) Effects of Soil Amendment on the Bioavailability of Lead, Zinc, and Cadmium to Earthworms. J. Environ. Qual., 29, 1611-1617.

Rao, J. V.; Rao, A. P. (2001) Effects of Lead Acetate on the Behaviour and Morphology of Earthworms Eisenia foetida. Indian J. Environ. Toxicol, 11,8-11.

Raymond, C. L.; Neuhauser, E. F.; Malecki, M. R. (1985) Factors Affecting the Vermistabilization Process. Water Res., 19 (10), 1311- 1317.

Spurgeon, D. J.; Svendsen, C; Rimmer, V. R.; Hopkin, S. P.; Weeks, J. M. (2000) Relative Sensitivity of Life Cycle and Biomarker Response in Four Earthworms Species Exposed to Zinc. Environ. Toxicol. Chem., 19, 1800-1808.

Sylvia, R. K.; Arme, C. (1982) Integumentary Uptake of Dissolved Organic Matter by Earthworms Lumbricidae. Pedobiologia, 23, 358- 366.

Sunil Kumar*, Vishal Sharma, R. V. Bhoyar, J. K. Bhattacharyya, Tapan Chakrabarti

National Environmental Engineering Research Institute, Nehru Marg, Nagpur, India.

* National Environmental Engineering Research Institute, Kolkata Zonal Laboratory, 1-8, Sector ‘C, East Kolkata, P.O. East Kolkata Township, Kolkata-700 107, West Bengal, India; e-mail: [email protected], [email protected].

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