- Regular Article
- Open Access
Arsenic accumulation by Pseudomonas stutzeri and its response to some thiol chelators
© The Japanese Society for Hygiene 2008
- Received: 5 March 2008
- Accepted: 12 May 2008
- Published: 4 July 2008
The aim of this study is to examine arsenic accumulation by Pseudomonas stutzeri and its response to some thiol chelators, DMPS and MiADMSA.
Determination of arsenic accumulation by Pseudomonas sp. was carried out using an atomic absorption spectrophotometer, a TEM and an EDAX. Arsenate reductase enzyme assay was carried out from a cell-free extract of Pseudomonas sp. The effect of chelating agents on arsenite accumulation was analyzed. Total cellular proteins were analyzed using 1-D SDS-PAGE.
Pseudomonas sp. exhibited a maximum accumulation of 4 mg As g−1 (dry weight). TEM and EDAX analysis showed the presence of As-containing electron-dense particles inside the cells. Data on arsenate reductase enzyme kinetics yielded a Km of 0.40 mM for arsenate and a Vmax of 5,952 μmol arsenate reduced per minute per milligram of protein. The chelating agents MiADMSA and DMPS were found to reduce the arsenic accumulation by 60 and 35%, respectively, whereas the presence of both chelating agents in medium containing cells pretreated with arsenite reduced it by up to 90%. The total protein profile of the cellular extract, obtained by 1-D SDS-PAGE, indicated five upregulated proteins, and three of these proteins exhibited differential expression when the cells were grown with MiADMSA and DMPS.
This study shows a new approach towards arsenic detoxification. A combination treatment with MiADMSA and DMPS may be useful for removing intracellular arsenic. The proteins that were found to be induced in this study may play an important role in the extrusion of arsenic from the cells, and this requires further characterization.
- Arsenic bioaccumulation
- Arsenate reductase
- Chelating agent
- Arsenic removal
- Arsenic-induced protein/s
The metalloid arsenic (As) is a member of group V of the periodic table and is thus classified as a heavy metal . Although arsenic is generally toxic to life, it has been demonstrated that microorganisms can use arsenic compounds as electron donors or electron acceptors, and that they can possess arsenic detoxification mechanisms [2–5]. Arsenic occurs in nature in four oxidation states (+5, +3, 0 and −3), with pentavalent arsenate [+5, As(V)] and trivalent arsenite [+3, As(III)] being the most common forms. Both forms are toxic: arsenite disrupts sulfhydryl groups of proteins and interferes with enzyme function, whereas arsenate acts as a phosphate analog and can interfere with phosphate uptake and transport. Arsenic, like other heavy metals, cannot be destroyed once it has entered the environment . Microorganisms have evolved a variety of mechanisms for coping with arsenic toxicity, including minimizing the amount of arsenic that enters the cell (e.g., through increased specificity of phosphate uptake), oxidizing the arsenite (through the activity of arsenite oxidase), or arsenite peroxidation with membrane lipids. Resistance to arsenic species in both Gram-positive and Gram-negative organisms results from energy-dependent efflux of either arsenate or arsenite from the cell, mediated by the ars operon [3–5]. Our earlier studies confirmed the existence of a bacterium with an arsC gene that is responsible for the conversion of As(V) to As(III) , which may be either extruded from the cells or sequestered in the intracellular compartment in its free form and/or in conjugation with glutathione (GSH) or other thiols. AQP7 and AQP9 conduct the transmembrane movement of the likely substrate, the neutral species As(OH)3, which may be considered an inorganic equivalent of glycerol . On the other hand, microorganisms take up As(III) through the glyceroporin membrane protein . It can be assumed that the aquaglyceroporin transport system found in mammalian cells may be similar to the transport system that facilitates arsenite uptake by bacterial cells.
Meso-2,3-dimercaptosuccinic acid (MiADMSA) and 2,3-dimercaptopropane-1-sulfonate (DMPS) have been considered promising antidotes to acute or chronic arsenic intoxication [10–11] due to the ability of their vicinal thiol groups to react with trivalent arsenicals, forming a saturated five-member heterocyclic ring . Therefore, we made an attempt to study the response of thiol chelating agents on arsenic accumulation using Pseudomonas sp. as a model system, which may help to improve understanding of the role of chelating agents in the arsenic detoxification mechanism.
Pseudomonas stutzeri that had been isolated and characterized in our lab, and which has the ability to grow in the presence of arsenic , was used for the present study. This bacterium has shown maximum tolerance levels of 50 mM for arsenate and 0.2 mM for arsenite, respectively. Na arsenate, Na meta-arsenite, NADPH, and DTT were procured from Sigma (St. Louis, MO, USA); DMPS and MiADMSA were a gift from Dr S.J.S. Flora, DRDE, Gwalior.
Growth kinetics for Pseudomonas sp.
Culture slants were made and kept at 4 °C. The bacteria were grown at 37 °C in nutrient broth medium with continuous shaking at 110 rpm in the orbital shaker for all of the given conditions (control, arsenic stress). Cells were harvested by centrifugation (5,000×g for 10 min) at different time intervals during the lag, log and the stationary phases. Optical density was measured after different time intervals at 600 nm using a Cary (Varian, Palo Alto, CA, USA) 50 UV-visible spectrophotometer. The growth rate constant (k) for the log phase of growth was determined by plotting the log10 of the optical density against time . Experiments were performed in triplicate and repeated three times.
Determination of arsenic accumulation by Pseudomonas sp.
Cells were harvested by centrifugation (5,000×g for 10 min) and the pH of the supernatant was measured. The cell pellets were washed 2–3 times with normal saline, dried, and then used in the measurements of arsenic accumulation. One-milliliter samples were taken at various time intervals for cell mass determination and for arsenic quantification.
Arsenate reductase enzyme assay
Pseudomonas sp. bacteria were grown to mid-log phase in 200 ml of NB medium supplemented with 50 mM of arsenate, harvested by centrifugation for 10 min at 5,000 rpm, and washed twice in 25 ml reaction buffer (10 mM Tris, pH 7.5, with 1 mM Na2EDTA and 1 mM MgCl2). The cells were resuspended in 5 ml of reaction buffer, disrupted by sonication and cell-free extract was prepared by centrifugation at 5,000×g for 10 min at 4 °C. Arsenate reductase activity was measured using a method based on NADPH oxidation . The reaction was initiated at 37 °C by mixing 50 μl of cell-free crude extract in 820 μl of reaction buffer, 20 μl of 10 mM DTT (final concentration 300 μM), and 50 μl of 3 mM NADPH (final concentration 0.15 mM). Arsenate concentrations of 200, 500 and 1 mM were assayed along with “no arsenic” for controls. Absorbance decreases at 340 nm were recorded as NADPH oxidization coupled to the reduction of arsenate to arsenite. Enzyme activity was calculated using a molar extinction coefficient of 6.2 × 103 for NADP+. The endogenous NADPH oxidation rate was subtracted from the arsenate-induced NADPH oxidation.
TEM and EDAX analysis
Pseudomonas sp. bacteria grown without (control) and with (experimental) 50 mM sodium arsenate were harvested and fixed for 2 h at room temperature in 4% glutaraldehyde and then washed four times at the stationary phase in 0.1 M phosphate buffer pH (7.2). Pre-embedding of bacterial cells was done in 4% agar, and small pieces (1–2 mm2) were cut from solidified agar blocks. These pieces were fixed overnight at 4 °C in 2% osmium tetroxide (OsO4) in phosphate buffer before being dehydrated with acetone and embedded in polyepoxy resin. Ultrathin sections were cut with an ultramicrotome (Reichert OMU3, Vienna, Austria) equipped with a diamond knife and then stained with uranyl acetate and lead citrate as contrasting agents. The sections were mounted on copper grids. Micrographs of both control (without arsenate) and experimental cells (treated with arsenate) were taken with a 2000FX II transmission electron microscope (TEM) (JEOL, Eching, Germany), operating at 200 kV. Energy-dispersive X-ray analysis (EDAX) of the cell pellets was performed with a Philips (Eindhoven, The Netherlands) XL-30 electron microscope equipped with an ESEM-TMP EDAX microanalysis system (Philips).
Use of chelating agents to remove arsenite from Pseudomonas sp.
Group 1: Arsenic control (bacterial cells grown with 0.2 mM arsenite prepared in nutrient broth medium and transferred into N saline for 4 h)
Group 2: Cells grown with 0.2 mM arsenite and then transferred into a medium containing DMPS (0.5 μg ml−1) for 4 h
Group 3: Cells grown with 0.2 mM arsenite and then transferred into a medium containing MiADMSA (0.5 μg ml−1) for 4 h.
Group 4: Cells grown with 0.2 mM arsenite and then transferred into a medium containing MiADMSA and DMPS (0.5 μg ml−1) for 4 h.
Group 5: Control (bacterial cells grown in nutrient broth medium)
One-milliliter samples were taken at various time points for cell mass determinations and for arsenic analysis, while 5 ml samples were taken after 24 h during the mid-log phase to evaluate the cellular protein profiles of all of the groups. SDS gel electrophoresis was performed as per the method of Laemmli .
The arsenic concentrations in all of the samples were measured using an atomic absorption spectrophotometer with an autosampler (AS-72, AAS PerkinElmer, Norwalk, CT, USA) and a graphite furnace (MHS) (Analyst 100, AAS PerkinElmer) following wet acid digestion of the bacterial cells. Pellets were dried at 90–100 °C to constant weight and digested with concentrated nitric acid using a microwave digestion system (Multiwave 3000, Anton Paar, Austria, Europe). Samples were brought to a constant volume before analysis.
Effect of arsenic on the growth kinetics of Pseudomonas sp.
Determination of the accumulation of arsenic by the bacterial isolate
Arsenate reductase activity
TEM and EDAX analysis
Use of chelating agents to remove arsenite from bacterial cells
Effect of chelating agents on the cellular protein profile
The effects of environmental arsenic on human health can be devastating. This aspect, together with the environmental ubiquity of arsenic, led to the evolution of arsenic defense mechanisms in every organism studied, from Escherichia coli to humans. Organisms take up As(V) via phosphate transporters and As(III) by glyceroporin membrane protein  or hexose transporters . As(V) is then reduced to As(III), which may be either extruded from the cells, sequestered in the intracellular compartment in its free form and/or in conjugation with glutathione (GSH) or other thiols. In this study we focused on arsenic uptake by Pseudomonas sp. and its response to some conventional thiol chelating agents like DMPS and MiADMSA.
Our isolate could grow in up to 50 mM arsenate and could maintain its character even after being grown for 3–4 generations in metal-free medium. The decrease in the growth rate in the presence of a high concentration of arsenic may be due to the association of this ion with the membrane fraction, resulting in an expanded membrane, which may increase the number of binding sites and make it less effective at transporting materials needed for growth . Macy et al.  reported that the increase in the external pH to 9.4 when organisms used acetate as an electron donor was linked to arsenate reduction. A number of organisms have been isolated that use arsenic as a terminal electron acceptor in anaerobic respiration . There is a decrease in growth rate under these conditions and an increase in the final pH of the medium from 7.2 to 9.2, suggesting that the reduction in growth caused by arsenate and the alkalization of the medium might be due to the reduction of arsenate to arsenite. The pH of the medium was not found to be altered when cells grown with arsenite.
Aquaglyceroporins have been shown to facilitate the uptake of As(III), including E. coli GlpF , S. cerevisiae Fps1p [19–20], mouse AQP7 , and AQP9 from rat  and humans . It can be assumed that the aquaglyceroporin transport system found in the mammalian cells may be similar to the transport system that facilitates arsenite uptake by bacterial cells. Pseudomonas sp. exhibited a maximum arsenic accumulation of 4 mg As g−1 in dry bacterial pellets after 18 h of growth when supplemented with 50 mM arsenate, which may be due to the intracellular sequestration of arsenic. The arsenate reductase activity was found to be maximum during the mid-log phase of growth, indicating the conversion of arsenate to arsenite, which may be the mechanism driving the intracellular removal of arsenite by these cells after 18 h of growth. TEM and EDAX analysis showed the presence of As-containing electron-dense particles inside the cells, confirming the intracellular accumulation of the metalloid anion by Pseudomonas sp.
Sodium 2,3-dimercaptopropane sulfonate (DMPS) is another analog of BAL and is mainly distributed in the extracellular space. It can enter cells through a specific transport mechanism. No major adverse effects on humans or animals have been reported after DMPS administration . The monoisoamyl ester of DMSA (MiADMSA; a C5 branched chain alkyl monoester of DMSA) has been found to be more effective than DMSA at reducing the cadmium and mercury burden [11, 22–24]. As(III), which is reduced form of As(V), may form conjugates with either glutathione (GSH) or another thiol. Cells of Pseudomonas sp. pretreated with arsenite have shown to reduce their arsenic accumulation when in the presence of DMPS and MiADMSA either individually or in combination, indicating the role of these chelators in the arsenic uptake mechanism. These chelating agents probably form complexes with the arsenic and these complexes can then be extruded from the cells, suggesting that DMPS and MiADMSA could be useful for the removal of arsenic. MiADMSA would be especially advantageous, as it possesses high reactivity toward arsenite. Chelating agents can also affect the specific transport of proteins like glyceroporin membrane protein, leading to a reduction in arsenite uptake by these cells, or it may act as a competitive inhibitor for arsenite, thus aiding in the removal of intracellular arsenic by Psudomonas sp. The ability of these bacteria to remove arsenic–chelate complexes from solution relies on the presence of specific As-chelator transporter proteins; this topic needs further characterization.
It is established that many microorganisms survive in the presence of toxic metals or metalloids by inducing the expression of an array of resistance proteins. The highly specific nature of these resistance mechanisms is the result of a cleverly designed genetic circuit that is tightly controlled by specific metalloregulatory proteins. Patel et al.  have recently reported on multiple physiological responses induced by arsenate stress in P. stutzeri which are not exclusively associated with the expression of classical arsenic resistance operons, indicating the probable role of these proteins in the arsenic resistance mechanism. The role of proteins in the mechanism of the resistance of P. fluorescens to heavy-metal-induced stress, such as from Cu, Co and Pb, was demonstrated by Sharma et al. . Our results indicate differential expression when cells grown with MiADMSA and DMPS either individually or in combination, indicating the probable role of these proteins in the intracellular efflux of arsenite, which require further detailed studies.
The removal of toxic components like arsenic is of great importance, not only because of the resulting decontamination but also because this removal is important to human welfare and for maintaining ecological balance. Its high accumulation of and tolerance toward arsenic indicates that P. stutzeri could be a suitable candidate for developing bioremediation processes. The similarity between the aquaglyceroporin transport system found in bacterial cells and mammalian cells facilitating arsenite uptake suggests that MiADMSA and DMPS may be useful for the removal of intracellular arsenic, although this subject requires further exploration.
The authors thank the Director of the Defence Research and Development Establishment, Government of India, Gwalior, India for financial support.
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