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Applied and Environmental Soil Science
Volume 2011 (2011), Article ID 218929, 7 pages
Comparative Genotoxicity of Cadmium and Lead in Earthworm Coelomocytes
1Biology Department, Faculty of Science, Silpakorn University, Nakorn Pathom 73000, Thailand
2Faculty of Agriculture and Life Science, Lincoln University, Canterbury, Lincoln 7647, New Zealand
Received 1 December 2010; Accepted 11 March 2011
Academic Editor: Marco Trevisan
Copyright © 2011 Ptumporn Muangphra and Ravi Gooneratne. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.
To determine genotoxicity to coelomocytes, Pheretima peguana earthworms were exposed in filter paper studies to cadmium (Cd) and lead (Pb) for 48 h, at concentrations less than the LC10—Cd: 0.09, 0.19, 0.38, 0.75, and 1.50 μg cm−2; Pb: 1.65, 3.29, 6.58, 13.16, and 26.32 μg cm−2. For Cd at 0.75 μg cm−2, in the micronucleus test (detects chromosomal aberrations), significant increases () in micronuclei and binucleate cells were observed, and in the comet assay (detects DNA single-strand breaks), tail DNA% was significantly increased. Lead was less toxic with minimal effects on DNA, but the binucleates were significantly increased by Pb at 3.29 μg cm−2. This study shows that Cd is more acutely toxic and sublethally genotoxic than Pb to P. peguana. Cadmium caused chromosomal aberrations and DNA single-strand breaks at 45% of the LC10 concentration. Lead, in contrast, did not induce DNA damage but caused cytokinesis defects.
Earthworms are primary decomposers of soil organic matter and, thus, aid in improving soil quality and fertility. Earthworms are a dominant component of the soil faunal biomass, providing 10–200 g m−2 . Because of their ecological importance, earthworms are now adopted as an indicator organism for the assessment of potential impact of chemicals to soil organisms.
In agricultural operations worldwide, there is increasing concern about widespread soil contamination by chemicals and heavy metals. Cadmium (Cd) and lead (Pb) are two of the more toxic heavy metals released into soil by industrial processes. They are of particular concern because they have no biological function but are toxic to living organisms and pose a risk to human and environmental health. In polluted soil, earthworms are exposed to these pollutants both dermally and through gastrointestinal tract absorption from soil. The earthworm immune system is generally sensitive to heavy metal exposure. Exposure of earthworms to chemicals via the dermal route affects coelomocytes directly and, therefore, have a major influence on the health of earthworms. Therefore, monitoring earthworm immune competence can be regarded as a more sensitive and early-warning biomarker of ecosystem health.
Inorganic Pb is classified as a group IIA carcinogen, which is a probable human carcinogen . Cd is classified as a group I human carcinogen  and an animal carcinogen . In addition, Cd interferes with DNA repair, which can lead to mutations  and eventually carcinogenesis . Therefore, assessment of DNA damage is an important aspect of toxicity testing. Earthworm coelomocytes play a significant role in earthworm immunity  and, therefore, are frequently used to assess genotoxicity.
The comet assay has been used as a sensitive tool to measure DNA damage in a variety of organisms [8–10], while the micronucleus test, a cytogenetic technique, has been used to detect chromosomal aberrations and nuclear abnormalities such as binuclei and micronuclei—these are well-established indicators of cytotoxicity and genetic toxicology, respectively [11, 12].
In order to better understand Cd and Pb toxicity on the earthworm Pheretima peguana, this study aimed to determine the minimum Cd and Pb concentrations that would cause genotoxicity via dermal route of exposure, by measuring immune competence as reflected by chromosomal aberrations and DNA damage to coelomocytes. The frequencies of coelomocyte micronuclei and binucleate cells were used to assess chromosomal aberrations and inhibition of cytokinesis, respectively. Tail DNA% and DNA tail length were measured by the comet assay to assess DNA single-strand breaks. The study sought to confirm that the comet assay and micronucleus test are tools that can be used in genotoxicity assessment of Cd and Pb for ecotoxicity risk comparison.
2. Materials and Methods
Pheretima peguana earthworms were sourced from a local dealer in Bangkok, Thailand. The worms were maintained in the laboratory using a stock soil (50% loamy topsoil, 30% composted leaves and 20% animal manure) at 28 ± 1°C, 65% humidity, with a 12-h light: 12-h dark photoperiod. Watermelons were added once a week to supplement the stock soil. Adult individuals (300–600 mg) with a well-developed clitellum were used in all experiments. Prior to the experiment, the worms were removed from the stock soil, rinsed with water, blotted on filter paper, and kept in the dark at 28 ± 1°C for 24-h to allow depuration of gut contents.
Cadmium chloride (CdCl2) and lead nitrate [Pb(NO3)2] (Sigma Aldrich Chemical Co.) were diluted in double-distilled water to achieve the desired concentrations. All reagents were of analytical grade and prepared in Milli-Q grade water. Whatman no. 1 filter paper was placed in flat glass containers (2 × 9 cm) and wetted with 3 mL each of either Cd or Pb solutions or distilled water (control).
2.3. Acute Toxicity Studies
The acute toxicity of Cd and Pb to earthworms was assessed in a filter paper contact test using five concentrations of each metal (n = 20 earthworms per concentration) selected based on preliminary studies. The final heavy metal concentrations per square centimeter of filter paper used in the experiment were Cd: 4.70, 5.85, 7.05, 8.23, 9.40, and 10.58 μg cm−2 and Pb: 32.90, 37.60, 42.30, 47.00, 51.70, and 56.40 μg cm−2. All experiments were carried out in the dark at 28 ± 1°C for 48-h. The percentage mortality was determined at 24-h and 48-h; worms were considered dead when they did not respond to touch of the anterior region. Results of the treatment groups were compared with the controls and analyzed using Probit analysis to calculate the 48-h LC10 and LC50 for Cd and Pb.
2.4. Sublethal Toxicity Studies
In a sublethal toxicity study, earthworms (n = 5 per concentration) were exposed for 48-h to Cd and Pb concentrations less than the 48-h LC10—Cd: 0.09, 0.19, 0.38, 0.75, 1.50 μg cm−2; Pb: 1.65, 3.29, 6.58, 13.16, 26.32 μg cm−2 filter paper. Distilled water was used as the control. After 48-h, worms from each concentration were removed from the filter paper, washed in distilled water, and blotted on a paper towel. The number of surviving earthworms and their body weights were recorded. Three worms exposed to each metal concentration were used to collect the coelomocytes as described below.
2.5. Harvesting Coelomocytes
Coelomic fluid containing coelomocytes was obtained from the coelomic cavity by the extrusion method of Eyambe et al. . Briefly, the earthworms were rinsed in 3 mL of saline extrusion medium containing 5% ethanol, 71.2 mM NaCl, 5 mM EGTA, 50.4 mM guaiacol glyceryl ether in a Petri dish, with pH adjusted to 7.3 with 1.0 M NaOH. Extruded cells were transferred to ice-cold Ca2+ free Lumbricus balanced salt solution (LBSS) containing 71.5 mM NaCl, 4.8 mM KCl, 1.1 mM MgSO47H2O, 0.4 mM KH2PO4, 0.3 mM Na2HPO4, and 4.2 mM NaHCO3 and pH adjusted to 7.3 with 1.0 M NaOH .
2.6. Coelomocyte Morphology and Cell Viability
Coelomocyte morphology was examined microscopically. Cells were counted in a haemocytometer and the cell concentration adjusted to 105 cells mL−1. Cell viability was determined using the trypan blue exclusion test, after mixing equal volumes of the coelomocyte suspension and a 0.5% (w/v) trypan blue (Sigma) solution. Cell viability always exceeded 95%.
2.7. Micronucleus Test
An aliquot of 10 μL of coelomic fluid from each earthworm at each metal concentration was smeared on a glass slide, using three slides for each concentration. When the fluid dried, the coelomocytes were fixed with a methanolic fixative solution for differential staining of cellular components (Wright Rapid Stain). A total of 3,000 small coelomocytes from three separate slides (1,000 cells per slide) per concentration were scored using a compound microscope (Olympus, CH 30) at 1,000x magnification to determine the micronuclei and binucleate frequencies. The remaining coelomic fluid was used for the comet assay.
2.8. Comet Assay
To detect coelomocyte DNA damage, alkaline lysis followed by alkaline single-cell gel electrophoresis was conducted. Three microgel slides were prepared for each metal concentration according to the protocol of Singh et al.  and modifications of S. A. Reinecke and A. J. Reinecke . All steps were conducted in dim light at 4°C to prevent additional DNA damage. An aliquot of 20-μL cell suspension was mixed with 75 μL of 0.5% (w/v in PBS, pH 7.3) low-melting agarose (LMA) at 40°C, and overlaid on a microscopic slide precoated with 100 μL of normal melting agarose and immediately closed with a cover glass. Agarose was allowed to solidify by keeping slides on ice packs for 1 min. Cover glasses were removed, and 0.5% low-melting agarose (prepared in 40 mM Tris-HCl, pH 10.0) was layered on the slide and covered with a cover glass. Slides were then transferred onto ice packs for 1 min. Cover glasses were removed and slides kept in high-salt lysis buffer (2.5 M NaCl, 100 mM EDTA, 10 mM Tris base, 1% Triton-X, pH 10.0) for the duration of 15 ± 1-h in the dark at 4°C to remove cellular proteins and liberate the damaged DNA. Lysis slides were then kept in a horizontal electrophoresis tank containing alkaline electrophoresis buffer (300 mM NaOH, 1 mM EDTA, pH > 13) for 20 min to allow unwinding of DNA and to express DNA single-strand breaks and alkali labile sites. Next, electrophoresis was carried out for 30 min at 12 V and 300 mA at 4°C. Slides were then neutralized with a 0.4 M Tris buffer (pH 7.5) thrice at 5 min intervals.
Slides were stained with 100 μL of 20 μg mL−1 ethidium bromide for 5 min and washed with deionized water to remove excess stain. The slides were examined under a Nikon eclipse 80i fluorescent microscope with filter block UV-2A (excitation filter 510–560 nm, dichroic mirror 575 nm, emission 590 nm). Images of comets were recorded using a digital camera (Nikon DXM 1200C) and analyzed with the software program LUCIA (Laboratory Universal Computer Image Analyzer). At least 100 nonoverlapping comets per slide were captured randomly at 400x magnification and scored for the comet parameters, namely, tail DNA (TD) % (expressed as the percent of fluorescent intensity in tail) and DNA tail length (TL) (the distance from nuclear center to the end of the comet tail).
2.9. Statistical Analysis
In the sublethal study, results are expressed as the mean and standard error of the mean from three earthworms. Significant differences between the results of the different treatment groups were determined using one-way ANOVA and Tukey’s multiple comparisons. When the normality failed, the Kruskal Wallis H test was performed.
3.1. Acute Toxicity Test
Total 48-h earthworm mortality in the control replicates was <10%, which complies with the validity criteria of the OECD test protocol. Significant toxic effects and deaths were observed with all tested heavy metal concentrations and were most marked at the highest tested concentrations: 10.58 μg cm−2 for Cd and 56.40 μg cm−2 for Pb (Figure 1). The 48-h LC10 and LC50 values for Cd were 1.65 and 6.09 μg cm−2, respectively (Figure 1(a)) and for Pb 26.64 and 43.43 μg cm−2 (Figure 1(b)). Thus, Cd was acutely more toxic than Pb to P. peguana.
3.2. Micronucleus Test
The frequency of binucleate cells at each concentration was higher than for micronuclei, compared with the controls. The frequencies of binucleates and micronuclei in coelomocytes were significantly higher at Cd concentrations of 0.75 μg cm−2 and above compared with the controls (Figure 2(a)). Thus, Cd caused cytokinesis failure and chromosomal aberrations in the form of binucleates and micronuclei, respectively, at a level slightly less than 50% of the 48-h LC10.
There was also a significant increase in binucleate coelomocytes at and above Pb concentrations of 3.29 μg cm−2, which is about 12.5% of the Pb 48-h LC10 for earthworms. In contrast to Cd, Pb had no significant effect on micronuclei formation even at a concentration close to the LC10 (Figure 2(b)).
At LC10, the frequencies of Cd- and Pb-induced binucleates were similar: 9.67 (Cd) and 10.67 (Pb) cells per 1,000 coelomocytes. However, at LC10, the Cd-induced micronuclei frequency of 4.67 per 1,000 coelomocytes was almost three times higher than that observed with Pb (1.67).
3.3. Comet Assay
The mean coelomocyte tail DNA% and to a lesser extent DNA tail length increased progressively with increasing Cd concentration (Figures 3(a) and 3(b)). Cadmium at 0.75 μg cm−2 filter paper concentration and above, tail DNA% of coelomocytes increased significantly () compared with the controls (Figure 3(a)). At the highest Cd concentration (1.50 μg cm−2, slightly below the LC10 concentration), there was a significant increase () in DNA tail length compared with the controls (Figure 3(b)).
The LC10 and LC50 values of Cd for earthworms were 15-fold and 7-fold lower, respectively, than those of Pb, indicating that Cd was more acutely toxic to P. peguana than Pb. The exposure time of 48-h to Cd used in the present study was adequate to induce coelomocyte DNA damage. This is in good agreement with Fourie et al.  who used the same exposure time and found tissue Cd accumulation and subsequent DNA damage in earthworms exposed to a slightly higher Cd concentration in artificial soil-water medium. However, Homa et al.  reported that at least 3 days is required for Cd to accumulate in significant concentration in coelomocytes for induction of stress response proteins in Eisenia fetida exposed to 1.32 μg cm−2 Cd (and Zn, Cu, Pb) in filter-paper contact tests.
Greater toxicity of Cd compared with Pb may be due to the differences in bioavailability and/or absorption and/or compartmentalization of the two metals in the earthworms. This is supported by the studies of Nahmani et al.  and Ma . Li et al.  have shown that in Eisenia fetida, about 80% of cellular Cd was in the cytosol and only 20% in the cell membrane. This is in contrast to Pb where 50% of Pb was located in the cell membrane and much less in the cytosol. This may be due to the fact that Pb2+ has a larger ionic radius (1.19 Å) compared with Cd2+ (0.97 Å), and therefore a greater diffusion of Cd ions into the coelomocytes, whereas most of the Pb2+ binds to the cell membrane with limited transport to the coelomocyte cytosol and hence minimal toxicity to the coelomocytes.
In the sublethal 48-h study, both Cd and Pb increased the binucleate coelomocytes. Binucleate cells occur due to a defect in cytokinesis, the process by which two daughter cells normally separate following cell division. Our results demonstrate that the Cd concentration (0.75 μg cm−2) required to induce binucleate coelomocytes was approximately 25% of that required for Pb (3.29 μg cm−2). This finding agrees well with the study of Conder and Lanno  who reported that Pb is only slightly toxic and relatively well tolerated by the coelomocytes, compared with Cd, due to sequestration of Pb by chlorogogue cells. Fugère et al.  reported that Pb was relatively well tolerated by the earthworm coelomocytes whereas Cd was relatively toxic with effects on both coelomocyte viability and phagocytosis. Moreover, Homa et al.  reported that coelomocytes are selectively sensitive to certain metal ions due to differential upregulation of metallothionein by these ions on exposure to a 1.32 μg cm−2 concentration of each metal.
Lead treatment did not affect micronuclei frequency even at the highest Pb exposure concentration of 26.32 μg cm−2 in the 48-h sublethal study. Since micronuclei occur as a short-term response to a genotoxic substance , their expression frequency depends more on the exposure dose than the exposure duration . The significant increase in binucleate coelomocytes when Pb concentration was at and above 3.29 μg cm−2 implies that 3.29 μg cm−2 (equivalent to approximately 12.5% of the 48-h LC10 value) can be regarded as a sublethal Pb dose. Pb appears to have a greater effect on cytokinesis than on chromosomes in earthworm coelomocytes.
A significant increase in micronuclei in earthworm coelomocytes, an indication of chromosomal aberrations during mitosis on exposure to Cd at 0.75 μg cm−2, equivalent to approximately 50% of the calculated 48-h LC10, can be regarded as a sublethal effect because in this experiment no earthworm deaths occurred at this concentration. The Cd-induced formation of micronuclei and binucleate cells in earthworm coelomocytes is in agreement with cytotoxic and genotoxic effects of Cd on mammals [22, 23]. Genotoxicity to earthworm coelomocytes at 48-h LC10 can be extrapolated as that exposure of earthworms even to a slightly Cd contaminated soil may result in genetic material damage in chromosomes and DNA, with consequences to earthworms and, hence, to the terrestrial ecosystem in general. On exposure to higher Cd concentrations, tail DNA% indicative of single-strand breaks progressively increased and was significantly greater at 0.75 μg cm−2 compared with the controls, confirming that Cd can induce DNA damage in earthworm coelomocytes at 50% of the 48-h LC10, a sublethal concentration. Even though Pb at the highest concentrations of 26.32 μg cm−2 at near-LC10 concentration did not show any significant damage to DNA in the comet assay—confirming that Pb, unlike Cd, is not genotoxic even at LC10 concentration in a 48-h study. In support of these results, most authors report that Cd induces DNA strand breaks, sister chromatid exchanges, and chromosome aberrations in plant, mammalian and human cells [24–26] at relatively low exposure and well below the 48-h LC10 concentration.
Several metals—chromium, nickel, cobalt, and arsenic—in addition to Cd have been shown to be carcinogenic to humans and experimental animals . There are several possible mechanisms by which Cd induces DNA strand breaks, including inhibition of repair enzymes . One reason for this inhibition could be the competition of Cd with zinc ions, which are essential for DNA polymerase activity. Besides, Cd might interfere with calcium-regulated processes that are involved in the regulation of DNA replication and repair. Snyder  and Ochi and Ohsawa  reported the involvement of reactive oxygen species in the generation of DNA single-strand breaks and that Cd-mediated chromosomal aberrations occur when intracellular glutathione decrease.
In this study, the DNA damage in P. peguana caused by Cd at 0.75 μg cm−2 concentration is lower than that reported by Fourie et al.  who concluded that a much higher Cd concentration of 20 mg L−1 (sublethal dose) is required to induce DNA damage in Aporrectodea caliginosa, Dendrodrilus rubidus, and Eisenia fetida in an artificial soil–water medium. Toxicity to a lower Cd concentration as observed in this study is a reflection of the sensitivity of P. peguana coelomocytes to Cd, but it is more likely because the earthworms in filter-paper tests are starved unlike those in a soil-water medium. It is also possible that a more heterogeneous coelomocyte population may be present in other earthworm species and therefore these are relatively more resistant than P. peguana to DNA damage.
In conclusion, LC10 and LC50 values of Cd for P. peguana earthworms were 15-fold and 7-fold lower, respectively, than for Pb, indicating that Cd was more toxic than Pb. Cadmium was genotoxic and affected cytokinesis of P. peguana coelomocytes at 45% of the 48-h LC10 concentration. Lead at LC10 concentration did not affect DNA, but at 12.5% (3.29 μg cm−2) of the LC10 concentration, it affected cytokinesis.
This project was funded by the Faculty of Science, Silpakorn University, Nakorn Pathom, Thailand.
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