Open Access

Bioaccumulation of total mercury in the earthworm Eisenia andrei

SpringerPlus20165:681

https://doi.org/10.1186/s40064-016-2282-6

Received: 1 March 2016

Accepted: 5 May 2016

Published: 20 May 2016

Abstract

Earthworms are a major part of the total biomass of soil fauna and play a vital role in soil maintenance. They process large amounts of plant and soil material and can accumulate many pollutants that may be present in the soil. Earthworms have been explored as bioaccumulators for many heavy metal species such as Pb, Cu and Zn but limited information is available for mercury uptake and bioaccumulation in earthworms and very few report on the factors that influence the kinetics of Hg uptake by earthworms. It is known however that the uptake of Hg is strongly influenced by the presence of organic matter, hence the influence of ligands are a major factor contributing to the kinetics of mercury uptake in biosystems. In this work we have focused on the uptake of mercury by earthworms (Eisenia andrei) in the presence of humic acid (HA) under varying physical conditions of pH and temperature, done to assess the role of humic acid in the bioaccumulation of mercury by earthworms from soils. The study was conducted over a 5-day uptake period and all earthworm samples were analysed by direct mercury analysis. Mercury distribution profiles as a function of time, bioaccumulation factors (BAFs), first order rate constants and body burden constants for mercury uptake under selected conditions of temperature, pH as well as via the dermal and gut route were evaluated in one comprehensive approach. The results showed that the uptake of Hg was influenced by pH, temperature and the presence of HA. Uptake of Hg2+ was improved at low pH and temperature when the earthworms in soil were in contact with a saturating aqueous phase. The total amount of Hg2+ uptake decreased from 75 to 48 % as a function of pH. For earthworms in dry soil, the uptake was strongly influenced by the presence of the ligand. Calculated BAF values ranged from 0.1 to 0.8. Mercury uptake typically followed first order kinetics with rate constants determined as 0.2 to 1 h−1.

Keywords

Bioavailability Bioaccumulation Bioaccumulation factor Humic acid Earthworms Soil Mercury

Background

Organic matter strongly affects the binding of mercury ions in the environment and affects the mobility and bioavailability of this metal in sediments (Gismera et al. 2007). Mercury (and also other metals) can be reintroduced into the aquatic systems if the solubility, mobility and bioavailability changes as a result of a change in different environmental factors such as pH, salt concentration, the presence of complexing agents, and temperature. Sediments can be a long-term source of Hg to surface waters. Sediments are an important location as storage reservoirs for elemental mercury and facilitate Hg methylation, resulting in high concentrations of the more toxic monomethylmercury (CH3Hg+) in organisms (Inza et al. 1997; Lawrence and Mason 2001; Burton et al. 2006; Windmöller et al. 2015).

The toxicity of Hg to terrestrial invertebrates and its effects on survival, reproduction and growth is not well documented although such information is important for risk assessment from Hg pollution in terrestrial ecosystems. The toxicity of Hg2+ is strongly linked to its affinity for the sulphydryl groups, which are found in most proteins (Gudbrandsen et al. 2007). Earthworms in particular, have the ability to bioaccumulate toxins and can concentrate them internally to high levels. In turn they form the basis of many food chains, thereby passing these high levels on to the wildlife that feed on them. This poses a serious risk of secondary poisoning of these predators due to bio-magnification (Kamitani and Kaneko 2007). Because of the intricate relationship between earthworms and the soil and its contaminants, they can serve as useful biological indicators of soil contamination (Veiga et al. 1999; Dai et al. 2004).

Earthworms eat their way through soil, digest it and deposit it as waste, thereby aerating and mixing the soil (Ernst et al. 2008). This process enhances the uptake of nutrients in the soil by plants. Earthworms can survive high-level of exposure by regularly crawling out of the exposure mixture. This practice decreases their contact time with the contaminated soil (Gudbrandsen et al. 2007). Bioaccumulation of Cu, Cd, Pb and Zn by earthworms is well documented and is thought to be in the chloragogenous tissue surrounding the posterior alimentary canal (Li et al. 2010). There are two pathways for the intracellular binding of metals in the chloragogenous tissue. The one pathway binds metals to insoluble, O-donating, phosphate-rich granules (chloragosomes) while the other pathway binds metals to low molecular, S-donating ligands (Sizmur and Hodson 2009). Uptake of Hg by earthworms could be by dermal route or uptake by the gut; the dermal route was however found to be more important, with more than 96 % of Hg found to be taken up by the dermal route (Hobbelen et al. 2006). Contamination in pore water is more available to earthworms for dermal uptake and thus uptake of metals is considered to be mainly via the dermal route. A different fraction of the heavy metal contaminants was present in the gut due to dietary intake because ingested materials are buffered to near neutral pH (Kamitani and Kaneko 2007). These studies typically report on the accumulation of heavy metals from contaminated soil but very few have measured uptake from water (Ernst et al. 2008; Sizmur and Hodson 2009; Calisi et al. 2013; Windmöller et al. 2015). As dermal uptake is very important, determining the accumulation of the metal fraction by water could provide strong evidence of metal mobility and availability (Sizmur and Hodson 2009). The bioavailability of pollutants in soil can be influenced by factors such as pH, cation exchange capacity as well as organic content. In previous reports where earthworms were placed in contaminant Cu bearing solutions, the focus was on differentiating between uptake via pore water and the dermal route (Arnold et al.2003; Steenbergen et al. 2005).

In the present study uptake of Hg by earthworms was quantitatively evaluated by placing earthworms in an aqueous/soil controlled microcosm as well as in a dry soil microcosm to assess uptake and bioaccumulation via the important dermal route as well as the gut route. The impact of dissolved HA on the bioavailability of Hg2+ was investigated under varying physical conditions of temperature and pH in controlled laboratory experiments.

Experimental

Test organism, study soil, aqueous phase and sample preparation

The experiment microcosm (2 L beaker) containing the aqueous phase, soil and earthworms were placed in a temperature controlled room and the experimental microcosms were exposed to a photo-period of 16 h of light (Fig. 1). The experimental set-up containing the aqueous phase required that air be bubbled through, for the preservation of the earthworms. The microcosms were also continually aerated after addition of the earthworms. The earthworms were not fed and the water was not changed in the microcosms over the 5 day duration of the experiments to avoid any factors associated with changes in soil geochemistry. Triplicate samples of all experiments were prepared and analysed separately by direct mercury analyser (DMA).
Fig. 1

Schematic diagram of the experiment to determine the uptake of Hg by earthworms in the presence of HA

The aqueous phase (Fig. 1a) was prepared by taking a saline solution, prepared from distilled water and NaCl to a final concentration of 35 µg/mL, spiking it with Hg2+ to 5 µg/mL. The pH of this solution was adjusted using acetic acid/ammonium buffer, 5.5, 7 and 8 respectively, in separate experiments as reported in Tables 2, 3 and 4. Soil pH, per se, was not measured as an experimental variable. After the aqueous phase was prepared, it was added on top of the soil layer and allowed to filter through and equilibrate, before the earthworms were introduced to the system.

Earthworms Eisenia andrei was the biota selected for the study of the uptake of Hg2+ in the presence of HA under different physical conditions. The earthworms were at least 6 weeks old adults of uniform size with well-developed clitella. They were allowed to depurate (the earthworms were left on damp filter paper in petri dishes without food to empty their guts) for 1 day before adding them to the experimental microcosms (30 earthworms/microcosm). During the experiment the earthworms were not fed, and in this way absorption via dermal and gut route was controlled to reflect only what was introduced to the microcosm for experimental purposes (Fig. 1b). After sampling the earthworms were not depurated as the experiment was designed to look at the distribution across all phases and gut content was part of the experimental data.

The soil layer (Fig. 1c) for each experiment was prepared by placing 6-cm layer (600 g) of previously cleaned soil in 2 L beakers. The HA solution, prepared from a soluble form of HA (Sigma Aldrich Catalogue number H1, 675-2 Lot.:S33786-057) was added to a final calculated concentration of 5 µg/g HA in the microcosm and left for 12 h to equilibrate at 4 °C, after which the aqueous phase and earthworms were added (wet microcosm). A control sample was prepared in the same way but without the addition of HA solution.

The sampling period of 5 days was based on a literature precedent from a similar investigation. Laboratory experiments carried out with amphipods, (Lawrence and Mason 2001) showed that a 6-day time period did not significantly affect invertebrate survival (>90 % average survival). The assumption was that treatment used in this study would not affect the percentage survival and growth of earthworms.

In a separate experiment (dry microcosm) 6-cm layer (600 g) of previously cleaned soil was placed in 2 L beakers (Fig. 2a). The soil was spiked with 0.5 µg/g Hg2+ as before and the same concentration HA was used in the 12 h equilibration at 4 °C, before the earthworms were added (Fig. 2b). The control sample for the dry microcosm was prepared in the same way but without adding the HA. Triplicate samples of all experiments was prepared and analysed separately by direct mercury analyser (DMA).
Fig. 2

Schematic diagram of the experiment to determine the uptake of Hg by earthworms in the presence of HA

Analytical procedures for determining the bioaccumulation Hg2+ in earthworms

The respective volume of water, soil and earthworm were collected and immediately frozen. All earthworm samples consisted of three earthworms randomly collected at each time interval. Triplicate samples of all phases (aqueous, soil and earthworms) were taken and analysed separately. The sampling period was 5 days; but most samples were taken and analysed within the first 2 days. First experiments in aqueous phase only which were recorded over a nine-day period indicated that most of the complexation took place within the first 48 h. Samples were stored in acid-cleaned Teflon storage containers and refrigerated until subsequent analysis. Analysis was performed using DMA for all samples, to obtain total Hg concentrations and to determine losses of Hg2+ from the experimental system.

The frozen samples were transferred to the analytical laboratory and analysed with DMA by the CSIR (Council for Scientific and Industrial Research; Natural Resources and Environment) as a paid service. It is the standard method employed by the CSIR for total mercury analysis. No pre-treatment of the sample was required and the method was suitable for solid and liquid samples. Because no digestion of the sample was needed there was no need for corrosive chemicals and the production of hazardous waste was minimal. The method also has a very good detection limit (Ipolyi et al. 2004). A dual cell atomic absorption spectrometer (AA) was used to determine elemental Hg absorption at a wavelength of 253.65 nm. Triplicate measurements were run on all of the samples, and standard reference materials were run between every 8 samples. A 0.2–0.5 g sample was placed into the sample boat, the sample was weighed, dried for a set period and then thermally decomposed. This process heated the sample to release the mercury and the vapours were carried by oxygen flow to an amalgamator for selective trapping of mercury on a gold trap. After a short heating period, the mercury released was measurement by atomic absorption (Ipolyi et al. 2004; Kading et al. 2009). The certified reference material used was Tort-2 and the Hg concentration found (237.37 ± 31.19) was in good agreement with the certified value at a 95 % confidence level.

Results and discussion

Determination of the complexation of Hg2+ with HA in aqueous phase, soil and earthworms at a fixed temperature of 293.15 K and variable pH

The complexation of Hg by earthworms in the absence of HA was done, at pH 5.5 only. For this control experiment, the Hg2+ concentration in aqueous phase was observed to decrease at the same time as the concentration of Hg2+ in the soil and the earthworms increased.

From the time based studies over a period of 48 h, the uptake of mercury followed a time dependent profile during the first 0–5 h. The distribution of mercury between soil, earthworms and aqueous phase in the control experiment, was clearly established by the trends observed from DMA analysis of the appropriate samples for mercury content (Fig. 3).
Fig. 3

Distribution of Hg2+ in aqueous phase, soil and earthworms at pH 5.5 at 293.15 K without any HA present. Earthworm and total Hg values are displayed on primary axis while the aqueous phase and soil values are on the secondary axis

The concentration of Hg2+ in the earthworms increased to a maximum of 74.1 %, within the first 1 h, after which a steady state was reached (Table 1). From the total amount of mercury available in the aqueous phase (5 µg/g), the maximum concentration of Hg2+ absorbed by earthworms was at 4 h (3.64 µg/g). The maximum adsorption measured for soil was 0.58 µg/g and the remaining Hg2+ in the aqueous was 0.12 µg/g. Hence, applying mass balance principles to the concentration distribution in earthworms at time = 1 h (79.2 %) and at time = 4 h (86.8 %) we can account for the total distribution of Hg2+ in the system (Hgaqueous phase + Hgsoil + Hgearthworms) (dotted line).
Table 1

DMA measurements of Hg2+ uptake control experiment for soil, earthworms and remaining in aqueous phase

pH values

Time (h)

Concentration (%) remaining in aqueous phase

Concentration (%) in soil

Concentration (%) in earthworms

pH 5.5

1

3.9

4.0

71.4

pH 5.5

4

2.4

11.6

72.8

pH 5.5

24

0.9

5.1

43.1

The complexation experiments were then repeated in the presence of HA, at three different pH values (5.5, 7.0 and 8.0) to observe the effect of pH on mercury uptake.

Following the same data analysis approach as for control experiment, the distribution of mercury between soil, earthworms and aqueous phase in the presence of HA, could account for 94.1 % (after 1 h) and 99.4 % (after 4 h) of the total Hg injected into the biosystem, initially (Fig. 4). Hence, we can account for the total distribution of Hg2+ in the system using the mass balance approach, based on measurements of Hg done by DMA (dotted line). The high correlation for mercury distribution is directly attributed to the complexation effect of the HA at pH 5.5 (Fig. 5).
Fig. 4

Distribution of Hg2+ in aqueous phase, soil and earthworms in the presence of HA at pH 5.5 at 293.15 K. Earthworm and total Hg (calc) values are displayed on primary axis while the aqueous phase and soil values are on the secondary axis

Fig. 5

Distribution of Hg2+ in earthworms in aqueous phase, at different pH values at 293.15 K (error bars represent SE, n = 3)

Similar distribution profiles for Hg in the presence of HA were obtained at pH 7.0 and 8.0. The proportion of Hg2+ in the different samples, at these pH values were tabulated as the mass balance distribution (Table 2).
Table 2

Distribution profile of Hg2+ in presence of HA in soil, earthworms and remaining in aqueous phase

pH values

Time (h)

Concentration (%) remaining in aqueous phase

Concentration (%) in soil

Concentration (%) in earthworms

pH 5.5

1

14.2

5.7

74.2

pH 5.5

4

10.9

9.5

79.0

pH 5.5

24

0.8

8.2

87.0

pH 7.0

1

3.5

4.8

74.3

pH 7.0

4

1.9

4.3

92.3

pH 7.0

24

0.64

5.4

84.0

pH 8.0

1

2.7

9.5

43.4

pH 8.0

4

1.1

12.0

78.1

pH 8.0

24

0.5

13.2

62.5

Accumulation of Hg2+ in earthworms was less effective at pH 8.0. pH has been identified from literature as being one of the most important parameters that determines uptake of Hg by earthworms (Burton et al. 2006; Ernst et al. 2008). At the beginning of these experiments absorption of Hg was attributed to absorption via the dermal route, due to the skin contact provided by the aqueous phase. However the fluctuation observed in absorption profiles over the extended time period, could be attributed to mixed absorption via dermal as well as the gut route, which are influenced by different physical parameters.

Determination of the complexation of Hg2+ with HA in soil and uptake by earthworms at different temperatures and ambient pH

In subsequent experiments the uptake of mercury by earthworms in dry soil, in the absence of the aqueous phase, was studied at 298.15 K and 303.15 K. The experimental set-up was the same but the aqueous phase was excluded. The Hg2+ concentration in the soil decreased while the concentration of Hg in the earthworms increased rapidly. The data showed an equilibrium condition between 4 and 24 h in the soil, a rapid increase between 24 and 28 h, and then a steady state condition (Figs. 6, 7). The accumulation of Hg2+ concentration in the earthworms after 48 h was best observed at 298.15 K, since the higher temperature resulted in expiration of the earthworms.
Fig. 6

Distribution of Hg2+ in soil and earthworms (dry experiment) at 298.15 K in the presence of HA

Fig. 7

Distribution of Hg2+ in soil and earthworms (dry experiment) at 303.15 K in the presence of HA

The distribution of mercury during 0–5 h between soil and earthworms were clearly established. From the total amount of mercury available in the soil (0.5 µg/g), the maximum concentration of Hg2+ absorbed by earthworms at 298.15 K after 48 h was (0.42 µg/g) and (0.16 µg/g) at 303.15 K. Accumulation of Hg2+ was thus higher at 298.15 K. Hence, applying mass balance principles to the concentration distribution in earthworms at 293.15 and 303.15 K at time = 1 h was (4.4 %) and (7.8 %) respectively and at time = 4 h (14.2 %) and (12.6 %) we can account for the total distribution of Hg2+ in the system (Hgsoil + Hgearthworms) (dotted line). The overall percentages for mercury distribution was again higher when the HA was added.

Accumulation of Hg in earthworms was faster and at higher concentration levels in the aqueous phase. The faster rates represent uptake of Hg2+ mainly via the dermal route. Hg distribution profiles based on mass balance of concentrations determined by DMA, account fully for the original value of Hg2+ introduced to the bio-system. The best distribution profile (99.4 % accountable) was obtained for aqueous phase experiment at pH 5.5 in the presence of HA. The best distribution profile for soil experiments (i.e. no aqueous phase) was found at lower temperature (84 %). In the soil experiments the absorption takes place mainly via the gut route.

Kinetics for the complexation of Hg2+ with HA in earthworms

Hg accumulation trends in earthworms, in the absence of HA (control study) was compared to the expected trend from literature (Veiga et al. 1999; Windmöller et al. 2015). The expected trend is an increase in Hg levels until a maximum after which the concentration remains constant, after which the earthworms expire (Gudbrandsen et al. 2007) (Fig. 8).
Fig. 8

Accumulation of Hg2+ in earthworms at 298.15 and 303.15 K without any HA present, in soil experiments (error bars represent SE, n = 3)

The control study confirmed that accumulation of Hg2+ in earthworms was favoured by lower temperature and represented uptake of Hg2+ mainly via the gut route. Hg absorption experiments, in the presence of HA, showed similar trends at 298.15 and 303.15 K, for accumulation of Hg2+ in earthworms up to 30 h after which the lower temperature evaluated, again showed a higher uptake of Hg via the gut route in presence of HA (up to 5 days) (Fig. 9).
Fig. 9

Hg levels in earthworms at 298.15 K (with HA added) and at 303.15 K (with added HA)

In the summary Table 3 the absorption of Hg by earthworms in the aqueous phase experiment (at time 48 h) was highest at 293.15 K at pH 5.5 (lower pH and temperature). For the dry soil experiments Hg absorption was improved at the lower temperature and in the presence of HA (Table 3).
Table 3

Summary of Hg2+ uptake by earthworms as a function of temperature and pH, at time 48 h

Aqueous phase present

Aqueous phase absent (dry soil experiment)

293.15 K

298.15 K

303.15 K

Control (without HA)

pH 5.5 (with HA)

pH 7.0 (with HA)

pH 8.0 (with HA)

Control (without HA)

Sample (with HA)

Control (without HA)

Sample (with HA)

75 %

75 %

75 %

48 %

34 %

84 %

11 %

33 %

The total percentage of Hg remaining in all phases was calculated and divided by the total value of Hg spiked (distribution profile) in an attempt to account for any loss of Hg due to absorption onto container walls or abiotic reduction, i.e. not related to absorption by earthworms and complexation by HA. In this way we have demonstrated that the distribution of Hg in a controlled environment can be fully accounted for. Highest losses were reported at high pH, high temperature and in the absence of HA (Table 4).
Table 4

Hg2+ percentage distribution profile, based on DMA analysis, at time 48 h

Aqueous phase present

Aqueous phase absent (dry soil experiment)

293.15 K

298.15 K

303.15 K

Control (without HA)

pH 5.5 (with HA)

pH 7.0 (with HA)

pH 8.0 (with HA)

Control (without HA)

Sample (with HA)

Control (without HA)

Sample (with HA)

82 %

82 %

80 %

62 %

55 %

99 %

36 %

55 %

Bioaccumulation factor of Hg in earthworms

Bioaccumulation factors (BAFs) can be used to estimate the bioavailability of metals to earthworm species (Nannoni et al. 2011). The U.S. Environmental Agency (2010) defined the Bioaccumulation factor as ‘The ration of the contaminant in an organism to the concentration in the ambient environment at a steady state, where the organism can take in the contaminant through ingestion with its food as well as through direct content’. It is calculated as the ratio of the Hg concentration in the earthworm (in µg/g dry wt) to the total soil Hg content (in µg/g dry wt) (Álvarez et al. 2004; Rodríquez Álvarez et al. 2014; Nannoni et al. 2011). Previous studies (Burton et al. 2006; Nannoni et al. 2011) found BAF to be <1 which is in agreement with value obtained in the present study (Table 5).
Table 5

Bioaccumulation factor of Hg by earthworms at different temperature and pHs after 48 h

Aqueous phase present

Aqueous phase absent (dry soil experiment)

293.15 K

298.15 K

303.15 K

Control (without HA)

pH 5.5 (with HA)

pH 7.0 (with HA)

pH 8.0 (with HA)

Control (without HA)

Sample (with HA)

Control (without HA)

Sample (with HA)

0.75

0.75

0.75

0.48

0.34

0.84

0.11

0.33

Rate constants for the complexation of Hg2+ with HA in earthworms, for first order reaction

Rate constants (k) (bioaccumulation rates) were calculated with first-order kinetic model (Gấrdfeldt 2003; Nannoni et al. 2011). A graph of ln conc vs time (h) was constructed and k evaluated from the slope. A good fit was obtained with r2 > 0.99 (Fig. 10).
Fig. 10

Rate constant of the bioaccumulation of Hg by earthworms with HA present at 298.15 K

Values obtained in this study ranged from 0.2 to 1 h−1. The highest values obtained were for rate constants calculated from low temperature and pH data for complexation of Hg2+ with HA present (Table 6).
Table 6

Summary table of rate constant (hr−1) calculated for all complexation of Hg with HA

Aqueous phase present

Aqueous phase absent (dry soil experiment)

293.15 K

298.15 K

303.15 K

Control (without HA)

pH 5.5 (with HA)

pH 7.0 (with HA)

pH 8.0 (with HA)

Control (without HA)

Sample (with HA)

Control (without HA)

Sample (with HA)

0.4 h−1

0.9 h−1

1 h−1

1 h−1

0.4 h−1

0.4 h−1

0.2 h−1

0.3 h−1

Body burden calculations in earthworm

The soil metal content has a huge impact on earthworm body burden. Regression models have been used to calculate the body burden of earthworms from contaminated soils. Body burden calculations relate metal concentrations to soil metal concentrations (Nahmani et al. 2007). Very few studies have been published on determination of the body burden of mercury from soil metal content, hence direct comparison is difficult. However, values for other heavy metals are available e.g. Cd = 0.47 ± 0.12 and Pb = 0.27 ± 0.15 (Nahmani et al. 2007). Predictions of body burden from soil metal content are log-linear regressions of the form:
$${\text{Log}}\,{\text{M}}_{\text{ew}} = a\log \,{\text{M}}_{\text{s}} + b$$
where Mew = concentration of metal in the earthworm (µg/g); Ms = concentration of metal in the soil (µg/g); a and b are constants.
Body burdens where calculated by plotting Mew versus Ms with a = slope and b = intercept (Nahmani et al. 2007). The slope of the regression equation is metal dependent (Corp and Morgan 1991; Heikens et al. 2001) (Fig. 11).
Fig. 11

Determination of body burden constants from soil Hg content

Following the literature precedent we have calculated values for a and b from the respective linear plot obtained for Hg2+. The values for b were observed to be relatively constant but greater variation was observed in the value for a. Variation in a could be due to the absence/presence of HA and the difference in temperature (Table 7).
Table 7

Body burden constants for the complexation of Hg with HA in dry experiments with earthworms at 298.15 K and 303.15 K

 

298.15 K

303.15

 

Control (without HA)

Sample (with HA)

Control (without HA)

Sample (with HA)

a

0.15 ± 0.07

0.10 ± 0.04

0.05 ± 0.02

0.38 ± 0.11

b

0.83

0.82

0.85

0.80

The values of a for body burden of Hg2+ at the lower temperature was comparable to values of a determined for other metal species. As noted before, the higher temperature was not tolerated well by the earthworms and resulted in early expiration and hence this factor could influence the body burden data.

Discussion

Earthworms are important bioindicators of soil contamination. Bioavailability of Hg depends on the speciation, which in turn determines the toxicity, transport, and residual time of the metal in the environment. Abiotic speciation is mainly due to mercury-ligand formation. Previous studies (Burton et al. 2006; Ernst et al. 2008) have found that earthworms could survive highly contaminated soil of up to 22 µg/g Hg and concentrations of up to 6.5 µg/g Hg have been found in earthworms. Colacevich et al. (2011) found that long term exposure of earthworms to Hg-contaminated soil of up to 1287 mg/kg dry wt did not cause earthworm mortality. The ability of earthworms to convert Hg2+ to MeHg was also indicated by the speciation results obtained by Santoyo et al. (2011). Veiga et al. (1999) and Kaschak et al. (2014) found that methylation could occur in the gut of earthworms, but upon analysis found only about 1 % MeHg in the total Hg in the tissues.

The detailed kinetic approach that was demonstrated in our work makes a noteworthy contribution to the understanding of the kinetics of mercury uptake by earthworms. Mercury distribution profiles as a function of time. Bioaccumulation factors (BAFs), first order rate constants and body burden constants for mercury uptake under selected conditions of temperature, pH as well as via the dermal and gut route were evaluated in one comprehensive approach. Body burden constants for mercury uptake by earthworms were determined in this work and are reported here for the first time, since no previous reports for reference values were found. This work therefore represents a major contribution to the available knowledge in the evaluation of mercury uptake by earthworms.

Conclusion

Trends in the uptake of Hg2+ by selected invertebrates, earthworms Eisenia andrei, were evaluated at different time interval, up to 5 days. Hg analysis of soil, water and earthworm samples was done using standard DMA method. Uptake of Hg by earthworms at 293.15 K was almost immediate, and concentration of up to 75 % of the original spiked value was found at pH 5.5 and pH 7.0 after 48 h. The control sample also showed the same swift uptake and high amount of Hg in the earthworms. The rate constant was determined to be 0.4 in the control sample. In the samples where HA was present in the biosystem, the rate constant was 0.8–1 and Hg accumulation was favoured by low pH and low temperature. The body burden constants determined, were in good agreement with values reported for other divalent metal species.

In the samples containing only the soil and earthworms (no aqueous phase) at 298.15 K the Hg uptake was higher (84 %) in the sample containing the HA than in the control (34 %). The rate of uptake was the same with rate constant of 0.4. The control sample (no HA added), thus showed a similar trend over time, but reduced concentration accumulation of HA. This data suggests that bioavailability of Hg is enhanced through complexation with HA, thereby increasing the uptake of Hg by earthworms. Total Hg unaccounted for was only 1 % at 297.15 K in the presence of HA, but 45 % in control at 48 h.

We have clearly demonstrated that the uptake of Hg was influenced by pH, temperature and HA as supported by calculated values of BAF (0.1–0.8) and rate constants from (0.2 to 1). The body burden of Hg was found to be a = 0.05–0.4 and b was found to be constant at 0.8. The higher temperatures and pH were not favourable for uptake of Hg2+ in earthworms or indeed survival of the earthworms.

Declarations

Authors’ contributions

SL is the PhD candidate who was the lead researcher carrying out the experimental work and prepared the first draft of the manuscript. AC was the principal investigator on the project responsible for conceptualizing the study, developing the research strategies and providing primary funding for the project. PB was responsible for data analysis and interpretation and co-ordinating the preparation of the final manuscript. All authors read and approved the final manuscript.

Acknowledgements

A special thanks to the Council for Scientific and Industrial Research (CSIR, Stellenbosch, South Africa), Natural Resources and the Environment unit, for DMA analysis.

Competing interests

The authors declare that they have no competing interests.

Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.

Authors’ Affiliations

(1)
SensorLab, Chemistry Department, University of the Western Cape
(2)
Faculty of Science, University of the Witwatersrand

References

  1. Álvarez FF, Rodríquez TR, Espinosa AJF, Dabán AG (2004) Physical speciation or arsenic, mercury, lead, cadmium and nickel in inhalable atmospheric particles. Anal Chim Acta 524:33–40View ArticleGoogle Scholar
  2. Arnold RE, Langdon CJ, Hodson ME, Black S (2003) Development of a methodology to investigate the importance of chemical speciation on the bioavailability of contaminants to Eisenia andrei. Pedobiologia 47:633–639Google Scholar
  3. Burton DT, Turley SD, Fisher DJ, Green DJ, Shedd TR (2006) Bioaccumulation of total mercury and monomethylmercury in the earthworm Eisenia fetida. Water Air Soil Pollut 170:37–54View ArticleGoogle Scholar
  4. Calisi A, Zaccarelli N, Lionetto MG, Schettino T (2013) Integrated biomarker analysis in the earthworm Lumbricus terrestris: application to the monitoring of soil heavy metal pollution. Chemosphere 90:2637–2644View ArticleGoogle Scholar
  5. Colacevich A, Sierra MJ, Borghini F, Millán R, Sanchez-Hernandez JC (2011) Oxidative stress in earthworms short- and long-term exposed to highly Hg-contaminated soils. J Hazard Mater 194:135–143View ArticleGoogle Scholar
  6. Corp N, Morgan AJ (1991) Accumulation of heavy metals from polluted soils by earthworm, Lumbricus rubellus: can laboratory exposure of ‘control’ worms reduce biomonitoring problems? Environ Pollut 74:39–52View ArticleGoogle Scholar
  7. Dai J, Becquer T, Rouiller JH, Reversat G, Berhard-Reversat F, Nahmani J, Lavelle P (2004) Heavy metal accumulation by two earthworm species and its relationship to total and DTPA-extractable metals in soils. Soil Biol Biochem 36:91–98View ArticleGoogle Scholar
  8. Ernst G, Zimmermann S, Christie P, Frey B (2008) Mercury, cadmium and lead concentrations in different ecophysiological groups of earthworms in forest soils. Environ Pollut 156:1304–1313View ArticleGoogle Scholar
  9. Gårdfeldt K, Munthe J, Strőmberg D, Lindqvist O (2003) A kinetic study on the abiotic methylation of divalent mercury in aqueous phase. Sci Total Environ 304:127–136View ArticleGoogle Scholar
  10. Gismera MJ, Procopio JR, Sevilla MT (2007) Characterization of mercury–humic acids interaction by potentiometric titration with a modified carbon paste mercury sensor. Electroanalysis 19(10):1055–1061View ArticleGoogle Scholar
  11. Gudbrandsen M, Sverdrup LE, Aamodt S, Stenersen J (2007) Short-term pre-exposure increases earthworm tolerance to mercury. Eur J Soil Biol 43:S261–S267View ArticleGoogle Scholar
  12. Heikens A, Peijnenburg WJGM, Hendriks AJ (2001) Bioaccumulation of heavy metals in terrestrial invertebrates. Environ Pollut 113:385–393View ArticleGoogle Scholar
  13. Hobbelen PHF, Koolhass JE, Van Gestel CM (2006) Bioaccumulation of heavy metals in the earthworms Lumbricus rubellus and Aporrectodea caliginosa in relation to total and available metal concentrations in field soils. Environ Pollut 144:639–646View ArticleGoogle Scholar
  14. Inza B, Ribeyre F, Maury-Brachet R, Boudou A (1997) Tissue distribution of inorganic mercury, methylmercury and cadmium in the Asiatic clam (Corbicula fluminea) in relation to the contaminant levels of the water column and sediment. Chemosphere 35(12):2817–2836View ArticleGoogle Scholar
  15. Ipolyi I, Massanisso P, Sposato S, Fodor P, Morabito P (2004) Concentration levels of total and methylmercury in mussel samples collected along the coasts of Sardinia Island (Italy). Anal Chim Acta 505:145–151View ArticleGoogle Scholar
  16. Kading TJ, Mason RP, Leaner JJ (2009) Mercury contamination history of an estuarine floodplain reconstructed from a 210Pb-dated sediment core (Berg River, South Africa). Mar Pollut Bull 59:116–122View ArticleGoogle Scholar
  17. Kamitani T, Kaneko N (2007) Species-specific heavy metal accumulation patterns of earthworms on a floodplain in Japan. Ecotoxicol Environ Saf 66:82–91View ArticleGoogle Scholar
  18. Kaschak E, Knopf B, Petersen JH, Bings NH, König H (2014) Biotic methylation of mercury by intestinal and sulfate-reducing bacteria and their role in mercury accumulation in the tissue of the soil-living Eisenia foetida. Soil Biol Biochem 69:202–211View ArticleGoogle Scholar
  19. Lawrence AL, Mason RP (2001) Factors controlling the bioaccumulation of mercury and methylmercury by the estuarine amphipod Lectocheirus plumulosus. Environ Pollut 111:217–231View ArticleGoogle Scholar
  20. Li L, Xu Z, Wu J, Tian G (2010) Bioaccumulation of heavy metals in the earthworm Eisenia fetida in relation to bioavailable metal concentrations in pig manure. Bioresour Technol 101(10):3430–3436View ArticleGoogle Scholar
  21. Nahmani J, Hodson ME, Black S (2007) A review of studies performed to assess metal uptake by earthworms. Environ Pollut 145:402–424View ArticleGoogle Scholar
  22. Nannoni F, Protano G, Riccobono F (2011) Uptake and bioaccumulation of heavy elements by two earthworm species from a smelter contaminated area in northern Kosovo. Soil Biol Biochem 43:2359–2367View ArticleGoogle Scholar
  23. Rodríquez Álvarez C, Jimènez Moreno M, Guzmán Bernado FJ, Rodríquez Martín-Doimeadios RC, Berzas Nevado JJ (2014) Mercury methylation, uptake and bioaccumulation by earthworm Lumbricus terrestris (Oligochaeta). Appl Soil Ecol 84:45–53View ArticleGoogle Scholar
  24. Santoyo MM, Flores CR, Torres AL, Wrobel K, Wrobel K (2011) Global DNA methylation in earthworms: a candidate biomarker of epigenetic risks related to the presence of metals/metalloids in terrestrial environments. Environ Pollut 159:2387–2392View ArticleGoogle Scholar
  25. Sizmur T, Hodson ME (2009) Do earthworms impact metal mobility and availability in soil? A review. Environ Pollut 157:1981–1989View ArticleGoogle Scholar
  26. Steenbergen NTTM, Iaccino F, De Winkel M, Reijnders L, Peijnenburg WJGM (2005) Development of a biotic ligand model and a regression model predicting acute copper toxicity to the earthworm Aporrectodea caliginosa. Environ Sci Technol 39:5694–5702View ArticleGoogle Scholar
  27. Veiga M, Hinton J, Lilly C (1999) Mercury in the Amazon: a comprehensive review with special emphasis on bioaccumulation and bioindicators. In: Proceedings of National Institute for Minamata Disease (NIMD) Forum 99, Minamata, JapanGoogle Scholar
  28. Windmöller CC, Durão Júnior WA, de Oliveira A, do Valle CM (2015) The redox processes in Hg-contaminated soils from Descoberto (minas Gerais, Brazil): implications for the mercury cycle. Ecotoxicol Environ Saf 112:201–211View ArticleGoogle Scholar

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