- freely available
Sensors 2011, 11(11), 10638-10663; doi:10.3390/s111110638
Abstract: Cadmium, as a hazardous pollutant commonly present in the living environment, represents an important risk to human health due to its undesirable effects (oxidative stress, changes in activities of many enzymes, interactions with biomolecules including DNA and RNA) and consequent potential risk, making its detection very important. New and unique technological and biotechnological approaches for solving this problems are intensely sought. In this study, we used the commonly occurring potential pathogenic microorganism Staphylococcus aureus for the determination of markers which could be used for sensing of cadmium(II) ions. We were focused on monitoring the effects of different cadmium(II) ion concentrations (0, 1.25, 2.5, 5, 10, 15, 25 and 50 μg mL−1) on the growth and energetic metabolism of Staphylococcus aureus. Highly significant changes have been detected in the metabolism of thiol compounds—specifically the protein metallothionein (0.79–26.82 mmol/mg of protein), the enzyme glutathione S-transferase (190–5,827 μmol/min/mg of protein), and sulfhydryl groups (9.6–274.3 μmol cysteine/mg of protein). The ratio of reduced and oxidized glutathione indicated marked oxidative stress. In addition, dramatic changes in urease activity, which is connected with resistance of bacteria, were determined. Further, the effects of cadmium(II) ions on the metabolic pathways of arginine, β-glucosidase, phosphatase, N-acetyl β-d-glucosamine, sucrose, trehalose, mannitol, maltose, lactose, fructose and total proteins were demonstrated. A metabolomic profile of Staphylococcus aureus under cadmium(II) ion treatment conditions was completed seeking data about the possibility of cadmium(II) ion accumulation in cells. The results demonstrate potential in the application of microorganisms as modern biosensor systems based on biological components.
Environmental pollution by xenobiotics is increasingly becoming a global issue. In connection with the growing ecosystem contamination by xenobiotics, it is therefore increasingly important to monitor their presence and promptly assess potential risks to humans . The United Nations Environment Programme (UNEP) aims at monitoring and removing cadmium from the environment . Over the last 15 years The Comprehensive Environmental Response, Compensation, and Liability Act (CERCLA) has permanently listed Cd as No. 7 (out of 275 species) in its priority list of hazardous materials . Cadmium’s fate in the environment is shown in Scheme 1. Cadmium in its elemental form is a soft, silver-white metal, which occurs with other elements in the Earth’s crust with average content of 0.13–0.2 g t−1 in the lithosphere. This element is naturally found in air, water resources and soil as complex oxides, sulphides, and carbonates in zinc, lead, and copper ores . Mining of iron and zinc ores, the burning of fossil fuels, plastics, dyes or road transport constitute the main sources of environmental cadmium pollution, and therefore the routes whereby it can enter the human food chain . In mining global cadmium production increased during the period from 1970 to 2004 from about 17,000 tonnes to about 22,000 tonnes. Over the last 15 years, global consumption has remained relatively constant, at around 20,000 tonnes. Improperly disposal of batteries is another source of cadmium pollution . In the atmosphere cadmium is mainly emitted to the atmosphere in particulate form. From combustion sources, cadmium may, however, be emitted partly as elemental gaseous cadmium, but as it is cooled, this cadmium is also quickly bound to particulate matter, so atmospheric transport of cadmium is governed by aerosol (particle) transport mechanisms.
Quite extensive data sets of cadmium concentrations in the water column exist for specific locations in the world’s oceans and for different years over the last two to three decades. Through the literature search performed for this review, however, no examples of modelling or other quantification of the general horizontal transport of cadmium—or any other heavy metals—with ocean currents have been identified. Only two examples of quantification of the exchange of heavy metals (lead and cadmium) with ocean currents between one specific ocean, the Arctic Ocean, and neighbouring oceans was identified. These examples suggest that ocean transport may be an important pathway. In addition, the presence of cadmium in ammonium and phosphorus fertilizers is other important entry route of cadmium into the soil [7,8]. The chemistry of cadmium is to a great extent controlled by pH. Cadmium may be adsorbed on clay minerals, carbonates or hydrous oxides of iron and manganese or may be precipitated as cadmium carbonate, hydroxide, and phosphate. Under acidic conditions cadmium solubility increases, and very little adsorption of cadmium by soil colloids, hydrous oxides, and organic matter takes place. Both toxicity and bioavailability of cadmium are influenced by soil characteristics. Although cadmium is ranked as non-essential heavy metal, it is already toxic to plants, animals and humans at low doses and acts as a cumulative poison [9,10]. Some cadmium compounds are relatively water soluble, mobile in soil and bioavailable, depending on the water and soil chemistries. It tends to bioaccumulate in organs such as the kidney and liver of vertebrates, but aquatic invertebrates and algae can also build up relatively high concentrations. Effects on birds and mammals are mainly due to kidney damage. In sea birds and marine mammals in particular, cadmium accumulates to relatively high levels. Microorganisms are very prone to such accumulation, however, this phenomenon makes it possible to use some microorganisms as a biosensor for detection of selected substances contaminating the environment . The mechanisms of metal accumulation by microorganisms are summarized in Figure 1: (1) metal resistance of microbes is accomplished by intra- and extracellular mechanisms; (2) metals can be excreted via efflux transport systems; (3) sequestering compounds of the cytosol can bind and detoxify metals inside the cell; (4) the release of chelators into the extracellular milieu leads to bound and fixed metals; (5) the structure of the cell envelope is prone to bind large amounts of metals by sorption thus preventing influx . A great number of heavy metal resistant bacteria such as Cupriavidus metallidurans and others, is known to possess efflux transporters that excrete toxic or overconcentrated metals [12–15].
For metal ions to have physiological or toxic effects, they must enter the bacterial cell. Microbial uptake systems have to be tightly controlled to be able to differentiate between structurally very similar metal ions. Microorganisms use fast and unspecific uptake systems driven by the chemiosmotic gradient across the cytoplasmic membrane of bacteria. Membrane transport of cadmium(II) ions at Staphylococcus aureus has been summarized in [13,16–18]. The toxicity of heavy metal ions inside the cell may occur through the displacement of essential metals from their native binding sites or through ligand interactions. Especially heavy metal cations with high atomic numbers, e.g., Hg(II), Cd(II) and Ag(I), tend to bind SH groups [12,13,19]. By binding to SH groups, the heavy metal ions may inhibit the activity and/or the functioning of sensitive enzymes. Cations can also be segregated into complex compounds by thiol-containing molecules while on the other hand some heavy metal ions may be reduced to less toxic oxidation states . A metal compound that can be reduced should be able to diffuse out of the cell. Most divalent heavy metal ions are accumulated within the cells by the fast and unspecific CorA (metal transport system) Mg(II) transport system . Accumulation of Cd(II) in Gram-positive bacteria leads to the expression of the CadA resistance system (Figure 1), which is located on plasmid p1258 and related plasmids [12,20–22]. Cation efflux is catalysed by the CadA protein, which is a P-type adenosine triphosphatase (ATPase). ATP serves as a source of energy for CadA-catalysed cadmium transport . It has also been found that amplification of Smt metallothionein (MT) locus increases cadmium resistance and deletion of Smt decreases resistance .
A biosensor is an analytical device comprising a biological recognition element (e.g., enzyme, receptor, DNA, antibody, or microorganism) in intimate contact with an electrochemical, optical, thermal, or acoustic signal transducer that together permit analyses of chemical properties or quantities .
Microorganisms are suitable as biosensors thanks to their fast “in situ” analysis because of rapid bacterial cell growth and dividing, adaptability, resilience, and their metabolic activity [25–34]. In terms of construction of biosensors, microorganisms are among the most promising biological materials, because each cell represents an independent individual, and is therefore usually more resistant and more durable as compared with cellular components and tissues organisms, which was experimentally demonstrated . Other advantages include the wide range of substances which cause a response, because of convergent metabolic pathways [33,36]. Generally, bacterial biosensors most frequently use electrochemical detectors as the amperometric [37,38], potentiometric , or conductometric  methods or optical detectors measuring bioluminescence , fluorescence  and/or colorimetric sensing . Microbial biosensors based on the detection of changes in pressure  or respiration  are less widely used. Microbial biosensors are well reviewed by Lei et al. . Microorganisms such as biosensors are widely used in healthcare, in control of foodstuffs , agriculture  or the environment . Using such biosensors can determine a wide range of organic compounds such , heavy metals [41,49] and other types of xenobiotics [36,39,43,50]. Microbial biosensors based on genetically modified microorganisms are other well developed area [51,52]. Bioreporters belong to the most promising, whose design uses two key genes that are responsible for producing a measurable signal and analyte-specific recognition and subsequent activation of reporter genes . Genes are based on contact with a chemical compound or changing physico-chemical conditions (pH, temperature, osmotic pressure, electric potential), activated when the activation leads to generation of a specific and easily measurable signal [54,55]. The use of bioreporters can be particularly advantageous in the detection of contaminated sites, where mixtures of different compounds occur, usually because bioreporters detect groups of related substances rather than individual chemicals .
The aim of this study was to demonstrate the principle and possibilities of metabolic signals (changes in growth, changes in the content of cadmium(II) ions, glutathione, metallothionein, free thiol moieties, activity of glutathione-S-transferase, total protein content, metabolism of sucrose, lactose, fructose, mannose, trehalose, N-acytyl-d-glucosamine, mannitol, urease, phosphatase and arginine) of Staphylococcus aureus as a biosensor to monitor cadmium(II) ions.
2. Experimental Section
All chemicals used (of ACS purity) were purchased from Sigma Aldrich (USA) unless noted otherwise. Cd(NO3)2 was used in our experiments as a source of cadmium(II) ions. Acetate buffer of pH 5 was prepared with 0.2 M acetic acid and 0.2 M sodium acetate and diluted with water and used as a supporting electrolyte. High purity deionised water (Milli-Q Millipore 18.2 MΩ/cm, Bedford, MA, USA) was used in the study.
2.2. Cultivation of Bacterial Strains
Staphylococcus aureus (NCTC 8511) was obtained from the Czech Collection of Microorganisms, Faculty of Science, Masaryk University, Brno, Czech Republic. Strains were stored as a spore suspension in 20% (v/v) glycerol at −20 °C. Prior to use in this study, the strains were thawed and the glycerol was removed by washing with distilled water. The bacterial strain was incubated in the presence of cultivation medium (meat peptone 5 g L−1, NaCl 5 g L−1, bovine extract 1.5 g L−1, yeast extract 1.5 g L−1 (HIMEDIA, Mumbai, India)), sterilized MiliQ water with 18 MΩ) at 600 rpm and 37 °C in Incubator Hood TH 15 (Edmund Buhler GmbH, Hechingen, Germany). pH of the cultivation medium was adjusted at 7.4 before sterilization. Sterilization was carried out at 121 °C for 30 min. in sterilizer (BMT, Brno, Czech Republic). Grown bacterial culture was diluted by cultivation medium to OD600 = 0.1 prior to use in the following experiments. The prepared medium (10 mL) was pipetted into 25 mL flasks and cadmium(II) ions (0, 1.25, 2.5, 5, 10, 15, 25 and 50 μg mL−1) were added.
2.3. Growth Curves
Solution containing bacteria, cultivation medium and various concentrations of cadmium(II) ions was mixed and pipetted into plastic tubes (3 mL) (AnalytikJena, Jena, Germany). Subsequently, a SPECORD 210 device (AnalytikJena) was used for measuring of the solution absorbance at a wavelength of 600 nm every 30 min for 24 h. A carousel for eight samples was used. All measurements were done in five replicates. The resulting absorbance were averaged and recalculated to the control variant, which represented 100%. Cuvette area was thermostated throughout the experiment to 37 °C (F12/ED Julabo, Seelbach, Germany). The SPECORD device was controlled by the WinASPECT Version 188.8.131.52 program package (AnalyticJena).
2.4. Preparation of Biological Samples
2.4.1. Spectrophotometric Measurements (Metabolic Parameters, Total Protein Content, Sulfhydryl Groups and Glutathione-S-Transferase) and Chromatographic Measurements (Reduced and Oxidized Glutathione)
The obtained cells were washed three times with phosphate buffer of pH 7. Weighed bacterial samples (approximately 0.1 g of fresh weight) were transferred to test-tube (2 mL) (Eppendorf, Hamburg, Germany), and liquid nitrogen was added. The samples were frozen to disrupt the cells. The mixture was prepared using a hand-operated ULTRA-TURRAX T8 homogenizer (IKA, Konigswinter, Germany) at 25,000 rpm for 3 min. The homogenate was transferred to a new test-tube. The mixture was further homogenised by shaking on a Vortex-2 Genie (Scientific Industries, New York, NY, USA) at 4 °C for 30 min. The homogenate was centrifuged (14,000 rpm) for 30 min at 4 °C using a Universal 32 R centrifuge (Hettich-Zentrifugen GmbH, Tuttlingen, Germany). Prior to analysis the supernatant was filtered through a membrane filter (0.45 μm Nylon filter disk, Millipore, Billerica, MA, USA).
2.4.2. Electrochemical Measurement (Cadmium)
Content of cadmium(II) ions was determined in medium and in bacteria as free (without mineralization) and bound (samples were mineralized). Medium. A sample (2 mL) in a test tube was centrifuged at 1,500 rpm for 15 min. (Eppendorf). The obtained supernatant was pipetted and 500 μL of the supernatant was used for the determination of Cd(II) in cultivation medium. Free cadmium(II) ions in bacteria. The obtained cells were washed three times with phosphate buffer of pH 7. After the last wash 0.1 M phosphate buffer (pH 7.0, 1.5 mL) was added. The prepared sample was ultrasounded for 2 min at 40 W using a needle probe (Bandelin, Berlin, Germany). Homogenates were then vortexed for 5 min at 400 rpm (Genie, New York, NY, USA) and then centrifuged for 15 min at 16,000 rpm (Eppendorf) prior to electrochemical analysis. Bound cadmium(II) ions in bacteria. The obtained cells were washed three times with phosphate buffer of pH 7. To prepare the samples microwave digestion were used according to recently published papers [15,57,58]. Briefly, the mineralization of samples took place in a microwave system Multiwave3000 (Anton-Paar GmbH, Graz, Austria). A sample (10 mg of bacteria) was placed into MG5 glass vials and (i) 350 μL of nitric acid (65%, w/w) and 150 μL of hydrogen peroxide (30%, w/w) or (ii) 700 μL of nitric acid (65%, w/w) and 300 μL of hydrogen peroxide (30%, w/w) were added. Prepared samples were sealed and placed into a 64MG5 rotor (Anton-Paar GmbH). The rotor with the samples was inserted into the microwave system and the microwave digestion was carried out under the following conditions: power 50 W—10 min, power 100 W—30 min, cooling (power 0 W)—10 min, maximum temperature 80 °C. Sample preparation for subsequent electrochemical measurements was as follows: 100 μL mineralized sample was pipetted into Eppendorf tubes with 900 μL acetate buffer (pH = 5.00). A blank digestion was simultaneously carried out in the same way.
2.4.3. Electrochemical Measurement (Metallothionein)
The obtained cells were washed three times with phosphate buffer of pH 7. Weighed bacterial samples (approximately 0.2 g of fresh weight) were transferred to test-tube (2 mL) (Eppendorf), and liquid nitrogen was added. The samples were frozen to disrupt the cells. The mixture was prepared using an ULTRA-TURRAX T8 hand-operated homogenizer (IKA) at 25,000 rpm for 3 min. The homogenate was transferred to a new test-tube and vortexed for 15 min at 4 °C (Vortex Genie). The supernatant was subsequently heat treated. The sample was kept at 99 °C in a thermomixer (Eppendorf, Hamburg, Germany) for 15 min. with occasional stirring, and then cooled to 4 °C. The denatured homogenates were centrifuged at 4 °C, 15,000 rpm for 30 min. (Eppendorf 5402). Heat treatment effectively denatures and removes high molecular weight proteins out from samples [59–61].
2.5. Determination of Metabolic Parameters
Determination of urease and phosphatase activities, and quantification of arginine, N-acetyl β-d-glucosamine, sucrose, trehalose, mannitol, maltose, mannose, lactose and fructose was performed on a Multiskan EX analyser (ThermoScientific, Waltham, MA, USA). For determination of activities and/or presence of all mentioned substances, kits purchased from the same company as analyser were used. The kits were used for on-line monitoring of these substances in living bacteria cultivated in the special well. Basic principles of measurements of the markers were as follows: urease: the enzyme urease hydrolyses urea to ammonia, arginine: l-argininedihydrolase hydrolyses l-arginine; phosphatase: phosphatase hydrolyses nitrophenylphosphate to inorganic phosphate and p-nitrophenyl, N-acetyl β-d-glucosamine, galactose, sucrose, trehalose, mannitol, mannose, lactose, fructose: they are used as a source of carbon and energy, during their decomposition acid reaction is formed and detected.
For measurements themselves, chemicals are pipetted in microplate wells. These plates also contained the above prepared bacterial solutions. Incubation was done at 37 °C (Thermostat, Biosan, Latvia). Samples were measured at a wavelength of 420 nm and 540 nm. Measurements were carried each 30 min for 24 h. The device was controlled by the Ascent Software Version 2.6 program package (ThermoScientific).
2.6. Determination of Total Protein Content, Sulfhydryl Groups and Glutathione-S-Transferase
Spectrophotometric measurements of total protein content, sulfhydryl groups and glutathione-S-transferase were carried using an automated chemical analyzer BS-200 (Mindray, Shenzhen, China). Reagents and samples were placed on cooled sample holder (4 ± 1 °C) and automatically pipetted directly into plastic cuvettes. Incubation proceeded at 37.0 ± 0.1 °C. Mixture was consequently stirred. The washing steps of pipetting needle with distilled water (18 mΩ) were done in the midst of the pipetting. The instrument was operated using the BS-200 software (Mindray).
2.6.1. Determination of Total Proteins Content
Determination of total proteins content using Bradford method is described in the following paper . Briefly, reagent Coomassie Brilliant blue G-250 (0.01% Coomassie Brilliant Blue G-250, 4.7% CH3CH2OH, 8.5% H3PO4, v/v) in volume of 190 μL was pipetted into cuvette. Further, sample (10 μL) was added. Mixture was incubated at 37 °C for 10 min. Absorbance was measured at 595 nm, reagent itself was used as a blank. Obtained values of absorbance (blank, mixture after 10 min long incubation) were used for determination of total proteins content. For calibration, bovine serum albumin (Sigma-Aldrich) was used.
2.6.2. Determination of Sulfhydryl Groups
Ellman’s spectrophotometric method was used for determination of sulfhydryl (-SH) moieties . Ellman’s reagent (277 μL, R1, 2 mM 5.5′-dithiobis(2-nitrobenzoic) acid (DTNB) in 50 mM sodium acetate CH3COONa) was mixed with sample (45 μL). Further, reagent R2 (33 μL, 1 M trisma base: CH3COOH) was added. Mixture was incubated at 37 °C for 10 min. Absorbance was measured at 405 nm. Values of absorbance of reagent R1 itself (blank) and mixture after 10 min. long incubation were used for determination of total-SH content.
2.6.3. Determination of Glutathione-S-Transferase
The method is based on glutathione-S-transferase (GST) catalysed reaction between reduced glutathione (GSH) and GST substrate, 1-chloro-2,4-dinitrobenzene (CDNB), which has the broadest range of isozyme detectability (e.g., alpha-, mu-, pi- and other GST isoforms). Under certain conditions, the interaction between glutathione and CDNB is dependent on the presence of active GST. The GST-catalysed formation of GS-DNB produces a dinitrophenylthioether, which can be detected spectrophotometrically at 340 nm . A 180 μL volume of reactants consisting of 2 mM CDNB and PBS (1.4 mM NaH2PO4, and 4.3 mM Na2HPO4, pH 7.4) (1:19, v/v, 37 °C) was added to sample in a plastic microtube. Further, 12.5 mM GSH (30 μL) in 0.1 M phosphate buffer (pH 7.4) was added. A wavelength of 340 nm was used for determination of GST activity.
2.7. Determination of Metallothionein
Differential pulse voltammetry (DPV) Brdicka reaction measurements were performed with a 747 VA Stand instrument connected to 746 VA Trace Analyzer and 695 Autosampler (Metrohm, Zofingen, Switzerland), using a standard cell with three electrodes and cooled sample holder (4 °C) according to protocol by Fabrik et al. . A hanging mercury drop electrode (HMDE) with a drop area of 0.4 mm2 was the working electrode. An Ag/AgCl/3M KCl electrode was the reference and glassy carbon electrode was auxiliary electrode. GPES 4.9 supplied by software EcoChemie was employed for smoothing and baseline corrections of the obtained data. A supernatant sample (200 μL) was pipetted into electrochemical cell containing 1,800 μL of Brdicka supporting electrolyte and measured using DPV. The electrolyte containing 1 mM Co(NH3)6Cl3 and 1 M ammonia buffer (NH3(aq) + NH4Cl, pH = 9.6) was used and changed per one analysis. DPV parameters were as follows: initial potential of −0.7 V, end potential of −1.75 V, modulation time 0.057 s, time interval 0.2 s, step potential 2 mV, modulation amplitude −250 mV, Eads = 0 V. All experiments were carried out at a temperature of 4 °C (Julabo F12 cooler).
2.8. Determination of Cadmium by Differential Pulse Voltammetry
Electrochemical analyser was used for determination of Cd(II) [25,65–67]. The analyser (757 VA Computrace, Metrohm AG, Zofingen, Switzerland) employs a conventional three-electrode configuration with a hanging mercury drop electrode (HMDE) working electrode: 0.4 mm2, Ag/AgCl/3MKCl as reference electrode, and a platinum auxiliary electrode. The following setup assembled of automated voltammetric analysis is supplied by Metrohm. An autosampler (Metrohm 813 Compact Autosampler) performs the sequential analysis of up to 18 samples in plastic test tubes. For the addition of standard solutions and reagents, two automatic dispensers (Metrohm 765 Dosimat) are used, while two peristaltic pumps (Metrohm 772 Pump Unit, controlled by Metrohm 731 Relay Box) are employed for transferring the rinsing solution in the cell and for removing solutions from the voltammetric cell. Differential pulse voltammetric measurements were carried out under the following parameters: deoxygenating with argon 90 s; deposition potential −0.8 V; time of deposition 240 s; start potential −0.8 V; end potential 0.15 V; pulse amplitude 0.025 V; pulse time 0.04 s; step potential 5.035 mV; time of step potential 0.4 s.
2.9. Determination of Reduced and Oxidized Glutathione
Reduced (GSH) and oxidized (GSSG) glutathione was determined using high performance liquid chromatography with electrochemical detection (HPLC-ED) . The chromatographic system consisted of two solvent delivery pumps operating in the range of 0.001–9.999 mL min−1 (Model 582 ESA Inc., Chelmsford, MA, USA), Zorbax eclipse AAA C18 (150 × 4.6; 3.5 μm particle size; Agilent Technologies, Santa Clara, CA, USA) and a CoulArray electrochemical detector (Model 5600A, ESA). The electrochemical detector includes three flow cells (Model 6210, ESA). Each cell consists of four working carbon porous electrodes, each one with auxiliary and dry Pd/H2 reference electrodes. Both the detector and the reaction coil/column were thermostated. The sample (20 μL) was injected using autosampler (Model 542 HPLC, ESA). Samples were kept in the carousel at 8 °C during the analysis. The column was thermostated at 32 °C. Mobile phase consisted of 80 mM TFA (A) and methanol (B). The compounds of interest were separated by the following linear gradient: 0 → 1 min (3% B), 1 → 2 min (10% B), 2 → 5 min (30% B), 5 → 6 min (98% B). Mobile phase flow rate of 1 mL/min, working electrode potential 900 mV. Time of analysis was 20 min.
2.10. Preparation of Deionised Water and pH Measurement
Deionised water was prepared using Aqual 25 reverse osmosis equipment (Sigma Aldrich, St. Louis, MO, USA). The deionised water was further purified by using apparatus MiliQ Direct QUV equipped with the UV lamp. The resistance was 18 MΩ. The pH was measured using pH meter Accurate 7110 (WTW inoLab, Weilheim, Germany).
2.11. Mathematical Treatment of Data and Estimation of Detection Limits
Mathematical analysis of the data and their graphical interpretation was realized by the Matlab (version 7.11) software. Results are expressed as mean ± standard deviation (S.D.) unless noted otherwise (EXCEL®). The detection limits (3 signal/noise, S/N) and quantification limits (10 S/N) were calculated according to Long and Winefordner , whereas N was expressed as standard deviation of noise determined in the signal domain unless stated otherwise. Accuracy, precision and recovery of cadmium(II) ions were evaluated with homogenates (bacterial samples) spiked with standards. Before extraction, 100 μL cadmium(II) ions standards and 100 μL water were added to bacterial samples. Homogenates were assayed blindly and cadmium(II) ions concentrations were derived from the calibration curves. Accuracy was evaluated by comparing estimated concentrations with known concentrations of heavy metals compounds. Calculation of accuracy (%Bias), precision (%C.V.), root mean square error (RMS error) and recovery was carried out as indicated according to Causon  and Bugianesi et al. . Equilibrium diagrams plotted using sophisticated algorithms (MEDUSA program) were used for the construction of a distribution diagram of different cadmium chemical forms present in the supporting electrolyte [72,73]. The basic parameters, including equilibrium constants that are necessary for the calculation of distribution diagrams are in the program database. The program author is Ignasi Puigdomenech from the Inorganic Chemistry of Royal Institute of Technology, Stockholm, Sweden. The MEDUSA program is freeware and is available on http://www.kemi.kth.se/medusa.
3. Results and Discussion
Transport of heavy metal ions in bacterial systems is not clear and requires further research. Bacterial sensors for detecting toxic substances including heavy metal ions belong to the areas receiving considerable attention. The reason for the use of living organisms as a sensor is the fact that living “bio” part of detection system is possible to obtain information of the effect of toxic substance on a cell together with obtaining the information about type of pollutant and its concentration.
3.1. Electrochemical Detection of Cadmium(II) Ions
The mercury drop electrode has been using for the determination of heavy metals since the discovery of polarography by Prof. Heyrovsky. The method is very simple and low cost and the technology is also easy to automate . In previously published papers, it is shown that cadmium ions can be detected well in acidic environments. Acetate buffer seems to be very suitable for this purpose, however, nature of the electrode process is not very clear [15,65]. To detect cadmium(II) ions, adsorptive stripping technique, in which heavy metals (cadmium) dissolve in mercury by forming amalgams, is used. Measurements are based on a preconcentration potential of −1.1 V (vs. Ag/AgCl) at a suitable deposition time, according to the following reaction: Cd2+ + ne− → Cd(Hg) and reoxidizing step these metal into the solution: Cd(Hg) → Cd2+ + ne− . Typical dependencies of peak height of cadmium(II) ions on their concentrations measured in the presence of acetate buffer pH 4, 5 and 6 are shown in Figure 2(A). The obtained calibration curves were linear within tested concentration interval from 0.25 nM to 100 nM and are shown in Table 1.
In addition, the effect of mineralization procedure (microwave digestion) on the obtained calibration dependence was investigated. Two variants were tested: (a) 700 μL HNO3 + 300 μL H2O2; (b) 350 μL HNO3 + 150 μL H2O2. The data was verified by analysing the sample digest of cadmium(II) ions in independent repetitions (n = 3) and, moreover, the effect of above mentioned pH 4, 5 and 6 of acetate buffer was tested. Recoveries of cadmium(II) ions varied within the interval from 98.5 to 100.5% in the tested samples. The obtained calibration dependencies measured in samples mineralized by both above mentioned procedures were strictly linear for (a) R2 = 0.9968 and (b) R2 = 0.9942. There were observed marked differences in mineralization process expressed as slopes of the calibration curves as (a) 5.8 and (b) 4.4. The difference is significant and means a decrease of analytical signal for more than 20%. Therefore, the mineralization variant (a) (350 μL HNO3 + 150 μL H2O2) was used in the following experiments.
The distribution of individual forms of cadmium complexes (at a concentration from 0 to 100 nM) in the presence of 200 mM acetate buffer of pH 5 is shown in Figure 2(B). Given our objective to study the effects of cadmium(II) ions on bacterial culture of S. aureus, it was necessary to monitor the effects of interactions between cadmium(II) ions and the cultivation medium (its composition is described in the Experimental Section and is a very complex matrix, hardly defined). Components of the medium react with cadmium(II) ions very intensely, as it is shown in Figure 2(C). Interactions between cadmium(II) ions and ions of cultivation medium was studied after 60 min. of their mixing at 20 °C. Cadmium(II) ion peak height measured in the presence of 100% cultivation medium decreased for more than 70% compared to cadmium(II) ions standard. Addition of medium to supporting electrolyte led to a shift of the peak height for 10 mV to more positive potentials (in upper inset in Figure 2(C)). The apparent interaction between the components of medium and cadmium(II) ions was expressed by slopes of the measured dependencies (Figure 2(C)). It is obvious that the linear model is less suitable for describing of dependencies shown in Figure 2(C). Confidence coefficients are higher than 0.98 (Table 2). Using a polynomial mathematical models seems to be more convenient (Table 1) due to the fact that confidence coefficients are higher than 0.99. Slopes of the dependencies decreased with the increasing content of cultivation medium for 2 nA per 1% of the medium. Decrease in the slope was faster within the range of the addition of medium from 1 to 50%, at higher levels of medium there was moderate decrease in slope (see in bottom inset in Figure 2(C)). There is still not enough attention paid to the issue of the interactions between the components of cultivation medium and the actual concentration of compound of interest. These changes should be taken into account when one may monitor heavy metals in the environment.
3.2. Detection of Cadmium(II) Ions in Bacterial Samples
The interactions between cadmium(II) ions and S. aureus are not fully understood . The resistance to cadmium connected with some plasmids and fragments called cadD and cadX regions was described . A phenotypic association between reduced susceptibility to zinc and methicillin resistance in S. aureus was recently reported. The authors showed that czrC encodes zinc and cadmium resistance in CC398 MRSA isolates, and that it is widespread in both humans and animals. Thus, resistance to heavy metals such as zinc and cadmium may play a role in the selection of methicillin resistance in S. aureus . These facts open up new possibilities for understanding the possible processes behind resistance of microorganisms to antibiotics. Sensor based monitoring can be beneficial to produce better technical ways of treating bacterial infections. In this study, after the above mentioned characterization and optimization steps, levels of cadmium(II) ions were determined in cultivation medium obtained after treatment of S. aureus with cadmium(II) ions as described in the Experimental section. The dependence of cadmium(II) ion content in cultivation medium is shown in Figure 3(A). As expected, the dependence is strictly linear, but the amount of free Cd(II) ranged between 23–30% of the total content of cadmium(II) ions added into the medium (green columns in Figure 3(A)).
In addition, contents of free and bound cadmium(II) ions in bacterial cells were determined. Figure 3(B) shows the change in free Cd(II) with the increasing applied concentration. The content of free Cd(II) increased up to dose of 250 μg Cd(II) in 25 mL of cultivation medium and, after that, the increase in free Cd(II) content was more gradual. The content of bound Cd(II) increased linearly with the applied concentration of Cd(II) (Figure 3(C)). The inset in Figure 3(C) shows the correlation between bound and free Cd(II) content. The observed dependence shows the two processes, which can be defined by the changes in the behaviour of cadmium(II) accumulation detected after exceeding of free Cd(II) content of 20 μg·mg−1 protein. Figure 3(D) summarizes the ratios between free and bound content of Cd(II) and content of Cd(II) in medium. The highest content Cd(II) was observed bound to the surface of S. aureus cell wall as it was expected. Moreover, Cd(II) content in bacterial cells decreased with the increasing applied concentration, which can be associated with triggering of a number of defence mechanisms against uptake of cadmium(II) ions.
3.3. Growth of S. aureus Treated with Cadmium(II) Ions
Growth of bacterial cells is among the important characteristics of the interactions between bacteria and toxic compounds. For this purpose, growth characteristics were monitored spectrophotometrically using OD measured at 605 nm.
At the beginning of the experiment bacterial culture growing for 24 h was used. From this bacterial culture, starting culture with OD 0.1 (104 cells per mL) was prepared. A marked increase in growth of S. aureus without the presence of Cd(II) was detected and this is shown in Figure 4(A).
Due to the additions of different concentrations of cadmium(II) ions, start of the exponential growth phase and lag phase were shifted. The applied concentration of Cd(II) (50 μg·mL−1) was significantly inhibitory for the bacterial culture of S. aureus used in this study. In addition, we plotted the growth expressed as OD (absorbance measured at 605 nm) measured in the end of the treatment (24 h). The obtained dependence is shown in Figure 4(B). The resulting changes in the intensity of growth shown in Figure 4(B) are similar to those for growth inhibition of S. aureus bacterial strain RN4220 . A mathematical model for the whole tested concentration range was used to describe dependence shown in Figure 4(B). The model had the following equation: y = 115.16e−0.106x, R2 = 0.932. In the concentration range from 0 to 30 μg of Cd(II) per mL, the dependence of the linear nature with the following equation y = −2.0537x + 70.016, R2 = 0.9641 was obtained and is shown in inset Figure 4(B). The obtained experimental data clearly shows that the bacterial culture used is very sensitive to the applied concentration of Cd(II) at levels greater than 30 μg·mL−1 and is well suited to assess environmental contamination by heavy metals.
Our aim was to characterize the bacterial culture used with regard to its potential application in biosensors. Therefore, we also studied a group of biologically important molecules. Molecules connected with thiol (–SH) metabolism were investigated first. Levels of GSH, GSSG and GSH/GSSG were monitored using well established high-performance liquid chromatography with electrochemical detection. Typical chromatograms of cell lysates of S. aureus treated with cadmium(II) ions are shown in Figure 5(A). GSH was detected at a retention time (RT): 4.8 min. and GSSG at RT = 5.9 min. Both signals were well separated and readily detectable. The amount of GSH increased with the increasing concentration of applied cadmium(II) ions linearly up to 20 μg·mL−1. After that the changes were more gradual and the course of the obtained dependence well fit with the polynomial model: y = −0.0557x2 + 5.098x − 0.4749, R2 = 0.987 (Figure 5(B)). Similarly, GSSG levels were changed, but GSSG level does not change in an organism without oxidative stress. It clearly follows from the results obtained that there are apparent dramatic increases in GSSG levels with the increasing applied concentration of cadmium(II) ions according to the following equation: y = −0.0081x2 + 0.9085x + 0.6926, R2 = 0.990 (24 h long cultivation, Figure 5(C)). Monitoring of oxidative stress in S. aureus is a very good indicator of environmental pollution with heavy metals. Moreover, GSH/GSSG ratio is also good indicator. From the point of view of the importance of both GSH and GSSG, the ratio above 9 shows good redox pool maintenance. Decreases of this ratio are a good indicator of oxidative stress in a cell and, therefore, indicates also the presence of some xenobiotics. It is not surprising that a ratio lower than 4 falls within the area of oxidative stress and lower than 2 means high oxidative stress with membrane damage and alteration of other biological functions (Figure 5(D)).
Metallothioneins (MT) as major proteins with heavy metals detoxification functions play an important role in protective mechanisms [65,78,79]. Typical Brdicka voltammograms of MT and MT-like proteins determined in Staphylococcus aureus are shown Figure 5(E). The catalytic signal called Cat2, which is used for quantification of proteins of interest [65,80–84], was detected at −1.55 V. The height of this peak was enhanced with the applied concentration of cadmium(II) ions according to the following equation: y = −0.006x2 + 0.8222x + 0.8527, R2 = 0.987.
Total proteins content directly corresponds to the activity of individual cells. In Figure 6(A) the dramatic decrease in total protein content at an applied concentration of cadmium(II) ions as low as 5 μg·mL−1 is clearly indicated. This decrease can be clearly associated with alteration of bacterial growth and, thus, with damage to some important biochemical pathways. Besides total proteins content, glutathione is a very important detoxifying molecule and must be activated by the enzyme called glutathione-S-transferase (GST). GST activity exhibited a behaviour similar to other thiol compounds, which means that the activity was enhanced with the increasing applied concentration of cadmium(II) ions according to the following equation: y = −1.5031x2 + 188.31x + 157.75, R2 = 0.988. The dependence is shown in Figure 6(B). Therefore, we also aimed to determine free –SH moieties. Their concentration was also enhanced with the increasing applied concentration of cadmium(II) according to the following equation: y = −0.0887x2 + 9.7638x + 7.4024, R2 = 0.987. The dependence is shown in Figure 6(C). Moreover, we attempted to correlate GST activity and concentration of free –SH moieties, which is shown in the inset in Figure 6(C). A strong correlation between these markers (R2 = 0.992) was found. Table 3 presents the correlation coefficients between levels of thiols. A strong link between the content of MT, GST, GSSG and –SH moieties was revealed. Correlation analysis revealed a strong positive correlation, because the correlation coefficients was always higher than R2 = 0.990. This can be clearly associated with simultaneous triggering of protective mechanisms due to the stress caused by cadmium(II) ions.
Monitoring of selected metabolic parameters was also an aim of this study. We examined sucrose, lactose, fructose, mannose, threalose, maltose, N-acetyl β-d-glucosamine, mannitol, urease, phosphatase and l-arginine-dihydrolase levels and the results are shown Figure 7(A–K), respectively.
Bacterial culture (100 μL, OD605 0.1) was pipetted into the wells of plates (STAPHYtest, Lachema). Then, cadmium(II) ions were added in the following final concentrations (0, 1.25, 2.5, 5, 10, 15, 25 and 50 μg mL−1). Concentration of the metabolites of interest was determined at 15 min intervals for 24 h. Then, these dependencies were plotted and the slopes of the linear regressions are shown in the insets in Figure 7. The main group of these parameters represent changes in sugar metabolism (sucrose, lactose, fructose, mannose, threhalose, malthose, N-acetyl-d-glucosamine, mannitol) and three enzymes: urease, phosphatase and l-arginine-dihydrolase. Marked differences were observed in mannose, malthose and mannitol metabolism (Figure 7). Similarly, changes were observed in the activity of urease. Some changes in sucrose, fructose, trehalose, phosphatase and l-arginine dihydrolase were also measured, but these can be used for biosensing only in limited intervals. Lactose and N-acetyl-d-glucosamine showed no significant changes and these markers are certainly not suitable for use in sensors (Figure 7).
Metal ions that tend to accumulate in organisms is one of the greatest problems associated with heavy metals in the environment. Heavy metals can be thus accumulate through the food chain with the top being represented by predators. Food chain networks in sea are one of the most highly damaged environments. Coastal fish (such as the smooth toadfish) and seabirds (such as the Atlantic puffin) are often monitored for the presence of such contaminants. Biosensors help to monitor food safety and quality and to detect environmental pollution. In this study, the obtained experimental data provides basic information on the possible use of a range of biomolecules produced by a bacterial cell (S. aureus strain) as markers of metal pollution together with the fact that S. aureus can be employed as part of a biosensor. This paper is mainly aimed at the finding of the appropriate low molecular mass compounds, which are produced in higher or lower concentrations in bacteria as a response to stress caused by the presence of heavy metal ions. The results can be used for sensing of these toxic ions by combining spectrometry and/or electrochemistry and living bacteria. These types of sensors are of great interest because of the possibility of on-line monitoring they offer.
The financial support from the following projects IGA MENDELU 2/2011(IGA-32-A2), INCHEMBIOL MSM0021622412 (INCH 3.2011.6.11) and CEITEC CZ.1.05/1.1.00/02.0068 is highly acknowledged. The authors would like to express their thanks to Petr Koudelka for technical assistance.
- Han, F.X.X.; Banin, A.; Su, Y.; Monts, D.L.; Plodinec, M.J.; Kingery, W.L.; Triplett, G.E. Industrial age anthropogenic inputs of heavy metals into the pedosphere. Naturwissenschaften 2002, 89, 497–504. [Google Scholar]
- UNEP. Lead (pb) and Cadmium (Cd) at the 26th Session of the Governing Council Nairobi 21 to 24 February 2011, Available online: http://www.unep.org/hazardoussubstances/LeadCadmium/ScientificReviews/PreparationforGC26/tabid/6749/Default.aspx (accessed on 16 September 2011).
- Agency for Toxic Substance and Disease Registry (ATSDR), US Toxicological Profile for Cadmium; Department of Health and Humans Services, Public Health Service, Centers for Disease Control: Atlanta, GA, USA; Available online: http://www.atsdr.cdc.gov/toxprofiles/tp5.pdf (accessed on 16 September 2011).
- Garrett, R.G. Natural sources of metals to the environment. Hum. Ecol. Risk Assess 2000, 6, 945–963. [Google Scholar]
- Johansson, C.; Norman, M.; Burman, L. Road traffic emission factors for heavy metals. Atmos. Environ 2009, 43, 4681–4688. [Google Scholar]
- Ohms, D.; Kohlhase, M.; Benczur-Urmossy, G.; Schadlich, G. New developments on high power alkaline batteries for industrial applications. J. Power Sources 2002, 105, 127–133. [Google Scholar]
- He, Q.B.; Singh, B.R. Crop uptake of cadmium from phosphorus fertilizers. 2. Relationship with extractable soil cadmium. Water Air Soil Pollut 1994, 74, 267–280. [Google Scholar]
- Mazen, A.; Faheed, F.A.; Ahmed, A.F. Study of potential impacts of using sewage sludge in the amendment of desert reclaimed soil on wheat and jews mallow plants. Braz. Arch. Biol. Technol 2010, 53, 917–930. [Google Scholar]
- Huff, J.; Lunn, R.M.; Waalkes, M.P.; Tomatis, L.; Infante, P.F. Cadmium-induced cancers in animals and in humans. Int. J. Occup. Environ. Health 2007, 13, 202–212. [Google Scholar]
- Haouem, S.; Najjar, M.F.; El Hani, A.; Sakly, R. Accumulation of cadmium and its effects on testis function in rats given diet containing cadmium-polluted radish bulb. Exp. Toxicol. Pathol 2008, 59, 307–311. [Google Scholar]
- Haferburg, G.; Kothe, E. Microbes and metals: Interactions in the environment. J. Basic Microbiol 2007, 47, 453–467. [Google Scholar]
- Nies, D.H. The cobalt, zinc, and cadmium efflux system CzcABC from alcaligenes-eutrophus functions as a cation-proton antiporter in Escherichia-coli. J. Bacteriol 1995, 177, 2707–2712. [Google Scholar]
- Nies, D.H. Microbial heavy-metal resistance. Appl. Microbiol. Biotechnol 1999, 51, 730–750. [Google Scholar]
- Nies, D.H. Efflux-mediated heavy metal resistance in prokaryotes. FEMS Microbiol. Rev 2003, 27, 313–339. [Google Scholar]
- Majzlik, P.; Strasky, A.; Adam, V.; Nemec, M.; Trnkova, L.; Zehnalek, J.; Hubalek, J.; Provaznik, I.; Kizek, R. Influence of zinc(II) and copper(II) ions on streptomyces bacteria revealed by electrochemistry. Int. J. Electrochem. Sci 2011, 6, 2171–2191. [Google Scholar]
- Nucifora, G.; Chu, L.; Misra, T.K.; Silver, S. Cadmium resistance from Staphylococcus aureus plasmid pi258 cada gene results from a cadmium-efflux atpase. Proc. Natl. Acad. Sci. USA 1989, 86, 3544–3548. [Google Scholar]
- Silver, S.; Nucifora, G.; Chu, L.; Misra, T.K. Bacterial-resistance atpases—Primary pumps for exporting toxic cations and anions. Trends Biochem. Sci 1989, 14, 76–80. [Google Scholar]
- Tynecka, Z.; Malm, A.; Skwarek, T. Effect of Cd2+ on growth of the cadmium-resistant and cadmium-sensitive Staphylococcus aureus. Acta Microbiol. Polonica 1989, 38, 117–129. [Google Scholar]
- Bruins, M.R.; Kapil, S.; Oehme, F.W. Microbial resistance to metals in the environment. Ecotoxol. Environ. Saf 2000, 45, 198–207. [Google Scholar]
- Novick, R.P.; Roth, C. Plasmid-linked resistance to inorganic salts in Staphylococcus aureus. J. Bacteriol 1968, 95, 1335–1342. [Google Scholar]
- Silver, S.; Walderhaug, M. Gene-regulation of plasmid-determined and chromosome-determined inorganic-ion transport in bacteria. Microb. Rev 1992, 56, 195–228. [Google Scholar]
- Tynecka, Z.; Gos, Z.; Zajac, J. Reduced cadmium transport determined by a resistance plasmid in Staphylococcus aureus. J. Bacteriol 1981, 147, 305–312. [Google Scholar]
- Turner, J.S.; Morby, A.P.; Whitton, B.A.; Gupta, A.; Robinson, N.J. Construction of Zn2+/Cd2+ hypersensitive cyanobacterial mutants lacking a functional metallothionein locus. J. Biol. Chem 1993, 268, 4494–4498. [Google Scholar]
- Gronow, M. Biosensors. Trends Biochem. Sci 1984, 9, 336–340. [Google Scholar]
- Huska, D.; Zitka, O.; Krystofova, O.; Adam, V.; Babula, P.; Zehnalek, J.; Bartusek, K.; Beklova, M.; Havel, L.; Kizek, R. Effects of cadmium(II) ions on early somatic embryos of norway spruce studied by using electrochemical techniques and nuclear magnetic resonance. Int. J. Electrochem. Sci 2010, 5, 1535–1549. [Google Scholar]
- Sochor, J.; Majzlik, P.; Salas, P.; Adam, V.; Trnkova, L.; Hubalek, J.; Kizek, R. A study of availability of heavy metal ions by using various exracction procedures and electrochemical detection. Lis. Cukrov. Repar 2010, 126, 414–415. [Google Scholar]
- Zitka, O.; Huska, D.; Adam, V.; Horna, A.; Beklova, M.; Svobodova, Z.; Kizek, R. Coularray detector as a tool for estimation of acute toxicity of silver(I) ions. Int. J. Electrochem. Sci 2010, 5, 1082–1089. [Google Scholar]
- Daunert, S.; Barrett, G.; Feliciano, J.S.; Shetty, R.S.; Shrestha, S.; Smith-Spencer, W. Genetically engineered whale-cell sensing systems: Coupling biological recognition with reporter genes. Chem. Rev 2000, 100, 2705–2738. [Google Scholar]
- Ramanathan, S.; Ensor, M.; Daunert, S. Bacterial biosensors for monitoring toxic metals. Trends Biotechnol 1997, 15, 500–506. [Google Scholar]
- Stocker, J.; Balluch, D.; Gsell, M.; Harms, H.; Feliciano, J.; Daunert, S.; Malik, K.A.; van der Meer, J.R. Development of a set of simple bacterial biosensors for quantitative and rapid measurements of arsenite and arsenate in potable water. Environ. Sci. Technol 2003, 37, 4743–4750. [Google Scholar]
- Badihi-Mossberg, M.; Buchner, V.; Rishpon, J. Electrochemical biosensors for pollutants in the environment. Electroanalysis 2007, 19, 2015–2028. [Google Scholar]
- Neufeld, T.; Schwartz-Mittelmann, A.; Biran, D.; Ron, E.Z.; Rishpon, J. Combined phage typing and amperometric detection of released enzymatic activity for the specific identification and quantification of bacteria. Anal. Chem 2003, 75, 580–585. [Google Scholar]
- Paitan, Y.; Biran, D.; Biran, I.; Shechter, N.; Babai, R.; Rishpon, J.; Ron, E.Z. On-line and in situ biosensors for monitoring environmental pollution. Biotechnol. Adv 2003, 22, 27–33. [Google Scholar]
- Biran, I.; Babai, R.; Levcov, K.; Rishpon, J.; Ron, E.Z. Online and in situ monitoring of environmental pollutants: Electrochemical biosensing of cadmium. Environ. Microbiol 2000, 2, 285–290. [Google Scholar]
- Biran, I.; Rissin, D.M.; Ron, E.Z.; Walt, D.R. Optical imaging fiber-based live bacterial cell array biosensor. Anal. Biochem 2003, 315, 106–113. [Google Scholar]
- Yong, D.M.; Liu, C.; Yu, D.B.; Dong, S.J. A sensitive, rapid and inexpensive way to assay pesticide toxicity based on electrochemical biosensor. Talanta 2011, 84, 7–12. [Google Scholar]
- Akyilmaz, E.; Dinckaya, E. An amperometric microbial biosensor development based on candida tropicalis yeast cells for sensitive determination of ethanol. Biosens. Bioelectron 2005, 20, 1263–1269. [Google Scholar]
- Lei, Y.; Mulchandani, P.; Chen, W.; Wang, J.; Mulchandani, A. Arthrobacter sp js443-based whole cell amperometric biosensor for p-nitrophenol. Electroanalysis 2004, 16, 2030–2034. [Google Scholar]
- Gaberlein, S.; Spener, F.; Zaborosch, C. Microbial and cytoplasmic membrane-based potentiometric biosensors for direct determination of organophosphorus insecticides. Appl. Microbiol. Biotechnol 2000, 54, 652–658. [Google Scholar]
- Bhatia, R.; Dilleen, J.W.; Atkinson, A.L.; Rawson, D.M. Combined physico-chemical and biological sensing in environmental monitoring. Biosens. Bioelectron 2003, 18, 667–674. [Google Scholar]
- Rensing, C.; Maier, R.M. Issues underlying use of biosensors to measure metal bioavailability. Ecotoxol. Environ. Saf 2003, 56, 140–147. [Google Scholar]
- Ben-Yoav, H.; Elad, T.; Shlomovits, O.; Belkin, S.; Shacham-Diamand, Y. Optical modeling of bioluminescence in whole cell biosensors. Biosens. Bioelectron 2009, 24, 1969–1973. [Google Scholar]
- Xu, Z.H.; Mulchandani, A.; Chen, W. Detection of benzene, toluene, ethyl benzene, and xylenes (btex) using toluene dioxygenase-peroxidase coupling reactions. Biotechnol. Prog 2003, 19, 1812–1815. [Google Scholar]
- Tzoris, A.; Fernandez-Perez, V.; Hall, E.A.H. Direct toxicity assessment with a mini portable respirometer. Sens. Actuat. B Chem 2005, 105, 39–49. [Google Scholar]
- Aivasidis, A.; Melidis, P.; Georgiou, D. Use of a microbial sensor: A new approach to the measurement of inhibitory effects on the microbial activity of activated sludge. Bioprocess. Biosyst. Eng 2002, 25, 29–33. [Google Scholar]
- Lei, Y.; Chen, W.; Mulchandani, A. Microbial biosensors. Anal. Chim. Acta 2006, 568, 200–210. [Google Scholar]
- Venugopal, V. Biosensors in fish production and quality control. Biosens. Bioelectron 2002, 17, 147–157. [Google Scholar]
- Krizkova, S.; Ryant, P.; Krystofova, O.; Adam, V.; Galiova, M.; Beklova, M.; Babula, P.; Kaiser, J.; Novotny, K.; Novotny, J.; et al. Multi-instrumental analysis of tissues of sunflower plants treated with silver(I) ions—Plants as bioindicators of environmental pollution. Sensors 2008, 8, 445–463. [Google Scholar]
- Adam, V.; Hanustiak, P.; Krizkova, S.; Beklova, M.; Zehnalek, J.; Trnkova, L.; Horna, A.; Sures, B.; Kizek, R. Palladium biosensor. Electroanalysis 2007, 19, 1909–1914. [Google Scholar]
- Olaniran, A.O.; Motebejane, R.M.; Pillay, B. Bacterial biosensors for rapid and effective monitoring of biodegradation of organic pollutants in wastewater effluents. J. Environ. Monit 2008, 10, 889–893. [Google Scholar]
- Busam, S.; McNabb, M.; Wackwitz, A.; Senevirathna, W.; Beggah, S.; van der Meer, J.R.; Wells, M.; Breuer, U.; Harms, H. Artificial neural network study of whole-cell bacterial bioreporter response determined using fluorescence flow cytometry. Anal. Chem 2007, 79, 9107–9114. [Google Scholar]
- Hassler, C.S.; Twiss, M.R.; McKay, R.M.L.; Bullerjahn, G.S. Optimization of iron-dependent cyanobacterial (synechococcus, cyanophyceae) bioreporters to measure iron bioavailability. J. Phycol 2006, 42, 324–335. [Google Scholar]
- Nivens, D.E.; McKnight, T.E.; Moser, S.A.; Osbourn, S.J.; Simpson, M.L.; Sayler, G.S. Bioluminescent bioreporter integrated circuits: Potentially small, rugged and inexpensive whole-cell biosensors for remote environmental monitoring. J. Appl. Microbiol 2004, 96, 33–46. [Google Scholar]
- Islam, S.K.; Weathers, B.; Terry, S.C.; Zhang, M.; Blalock, B.; Caylor, S.; Ripp, S.; Sayler, G.S. Genetically-engineered whole-cell bioreporters on integrated circuits for very low-level chemical sensing. Proceedings of the 35th European Solid-State Device Research Conference, ESSDERC ’05, Grenoble, France, 12–16 September 2005; Ghibaudo, G., Skotnicki, T., Cristoloveanu, S., Brillouet, M., Eds.; IEEE: New York, NY, USA, 2005; pp. 351–354. [Google Scholar]
- Bolton, E.K.; Sayler, G.S.; Nivens, D.E.; Rochelle, J.M.; Ripp, S.; Simpson, M.L. Integrated cmos photodetectors and signal processing for very low-level chemical sensing with the bioluminescent bioreporter integrated circuit. Sens. Actuat. B Chem 2002, 85, 179–185. [Google Scholar]
- Trogl, J.; Kuncova, G.; Kubicova, L.; Parik, P.; Halova, J.; Demnerova, K.; Ripp, S.; Sayler, G.S. Response of the bioluminescent bioreporter Pseudomonas fluorescens HK44 to analogs of naphthalene and salicylic acid. Folia Microbiol 2007, 52, 3–14. [Google Scholar]
- Hansen, T.H.; Laursen, K.H.; Persson, D.P.; Pedas, P.; Husted, S.; Schjoerring, J.K. Micro-scaled high-throughput digestion of plant tissue samples for multi-elemental analysis. Plant Methods 2009, 5, 12:1–12:11. [Google Scholar]
- Hynek, D.; Prasek, J.; Pikula, J.; Adam, V.; Hajkova, P.; Krejcova, L.; Trnkova, L.; Sochor, J.; Pohanka, M.; Hubalek, J.; et al. Electrochemical analysis of lead toxicosis in vultures. Int. J. Electrochem. Sci 2011. in press.. [Google Scholar]
- Fabrik, I.; Krizkova, S.; Huska, D.; Adam, V.; Hubalek, J.; Trnkova, L.; Eckschlager, T.; Kukacka, J.; Prusa, R.; Kizek, R. Employment of electrochemical techniques for metallothionein determination in tumour cell lines and patients with a tumor disease. Electroanalysis 2008, 20, 1521–1532. [Google Scholar]
- Adam, V.; Baloun, J.; Fabrik, I.; Trnkova, L.; Kizek, R. An electrochemical detection of metallothioneins at the zeptomole level in nanolitre volumes. Sensors 2008, 8, 2293–2305. [Google Scholar]
- Erk, M.; Ivankovic, D.; Raspor, B.; Pavicic, J. Evaluation of different purification procedures for the electrochemical quantification of mussel metallothioneins. Talanta 2002, 57, 1211–1218. [Google Scholar]
- Bradford, M.M. A rapid and sensitive method for the quantitation of microgram quantities of protein utilizing the principle of protein-dye binding. Anal. Biochem 1976, 72, 248–254. [Google Scholar]
- Ellman, G.L. Tissue sulfhydryl groups. Arch. Biochem. Biophys 1959, 82, 70–77. [Google Scholar]
- Park, H.; Choung, Y.K. Degradation of antibiotics (tetracycline, sulfathiazole, ampicillin) using enzymes of glutathione S-transferase. Hum. Ecol. Risk Assess 2007, 13, 1147–1155. [Google Scholar]
- Adam, V.; Fabrik, I.; Kohoutkova, V.; Babula, P.; Hubalek, J.; Vrba, R.; Trnkova, L.; Kizek, R. Automated electrochemical analyzer as a new tool for detection of thiols. Int. J. Electrochem. Sci 2010, 5, 429–447. [Google Scholar]
- Krystofova, O.; Trnkova, L.; Adam, V.; Zehnalek, J.; Hubalek, J.; Babula, P.; Kizek, R. Electrochemical microsensors for the detection of cadmium(II) and lead(II) ions in plants. Sensors 2010, 10, 5308–5328. [Google Scholar]
- Prasek, J.; Adamek, M.; Hubalek, J.; Adam, V.; Trnkova, L.; Kizek, R. New hydrodynamic electrochemical arrangement for cadmium ions detection using thick-film chemical sensor electrodes. Sensors 2006, 6, 1498–1512. [Google Scholar]
- Diopan, V.; Stejskal, K.; Galiova, M.; Adam, V.; Kaiser, J.; Horna, A.; Novotny, K.; Liska, M.; Havel, L.; Zehnalek, J.; et al. Determination of plant thiols by liquid chromatography coupled with coulometric and amperometric detection in lettuce treated by lead(II) ions. Electroanalysis 2010, 22, 1248–1259. [Google Scholar]
- Long, G.L.; Winefordner, J.D. Limit of detection. Anal. Chem 1983, 55, A712–A724. [Google Scholar]
- Causon, R. Validation of chromatographic methods in biomedical analysis—Viewpoint and discussion. J. Chromatogr. B 1997, 689, 175–180. [Google Scholar]
- Bugianesi, R.; Serafini, M.; Simone, F.; Wu, D.Y.; Meydani, S.; Ferro-Luzzi, A.; Azzini, E.; Maiani, G. High-performance liquid chromatography with coulometric electrode array detector for the determination of quercetin levels in cells of the immune system. Anal. Biochem 2000, 284, 296–300. [Google Scholar]
- Jagner, D.; Ma, F.; Wang, Y.D. Rapid calibration-free determination of lead in microliter amounts of whole blood. Electroanalysis 1996, 8, 952–954. [Google Scholar]
- Puigdomenech, I.; Bergstrom, U. Calculation of distribution coefficients for radionuclides in soils and sediments. Nucl. Saf 1995, 36, 142–154. [Google Scholar]
- Yarnitzky, C.N. The use of recycled static mercury drop electrode for electroanalysis of heavy metals in industrial wastes. Rev. Anal. Chem 2000, 19, 319–329. [Google Scholar]
- Ghoneim, M.M.; Hassanein, A.M.; Hammam, E.; Beltagi, A.M. Simultaneous determination of Cd, Pb, Cu, Sb, Bi, Se, Zn, Mn, Ni, Co and Fe in water samples by differential pulse stripping voltammetry at a hanging mercury drop electrode. Fresenius J. Anal. Chem 2000, 367, 378–383. [Google Scholar]
- Massidda, O.; Mingoia, M.; Fadda, D.; Whalen, M.B.; Montanari, M.P.; Varaldo, P.E. Analysis of the beta-lactamase plasmid of borderline methicillin-susceptible Staphylococcus aureus: Focus on bla complex genes and cadmium resistance determinants cadD and cadX. Plasmid 2006, 55, 114–127. [Google Scholar]
- Cavaco, L.M.; Hasman, H.; Stegger, M.; Andersen, P.S.; Skov, R.; Fluit, A.C.; Ito, T.; Aarestrup, F.M. Cloning and occurrence of czrc, a gene conferring cadmium and zinc resistance in methicillin-resistant Staphylococcus aureus CC398 isolates. Antimicrob. Agents Chemother 2010, 54, 3605–3608. [Google Scholar]
- Eckschlager, T.; Adam, V.; Hrabeta, J.; Figova, K.; Kizek, R. Metallothioneins and cancer. Curr. Protein Pept. Sci 2009, 10, 360–375. [Google Scholar]
- Ryvolova, M.; Krizkova, S.; Adam, V.; Beklova, M.; Trnkova, L.; Hubalek, J.; Kizek, R. Analytical methods for metallothionein detection. Curr. Anal. Chem 2011, 7, 243–261. [Google Scholar]
- Petrlova, J.; Potesil, D.; Mikelova, R.; Blastik, O.; Adam, V.; Trnkova, L.; Jelen, F.; Prusa, R.; Kukacka, J.; Kizek, R. Attomole voltammetric determination of metallothionein. Electrochim. Acta 2006, 51, 5112–5119. [Google Scholar]
- Fabrik, I.; Kukacka, J.; Baloun, J.; Sotornik, I.; Adam, V.; Prusa, R.; Vajtr, D.; Babula, P.; Kizek, R. Electrochemical investigation of strontium-metallothionein interactions—Analysis of serum and urine of patients with osteoporosis. Electroanalysis 2009, 21, 650–656. [Google Scholar]
- Huska, D.; Fabrik, I.; Baloun, J.; Adam, V.; Masarik, M.; Hubalek, J.; Vasku, A.; Trnkova, L.; Horna, A.; Zeman, L.; et al. Study of interactions between metallothionein and cisplatin by using differential pulse voltammetry Brdicka’s reaction and quartz crystal microbalance. Sensors 2009, 9, 1355–1369. [Google Scholar]
- Krizkova, S.; Blahova, P.; Nakielna, J.; Fabrik, I.; Adam, V.; Eckschlager, T.; Beklova, M.; Svobodova, Z.; Horak, V.; Kizek, R. Comparison of metallothionein detection by using of Brdicka reaction and enzyme-linked immunosorbent assay employing chicken yolk antibodies. Electroanalysis 2009, 21, 2575–2583. [Google Scholar]
- Krizkova, S.; Fabrik, I.; Adam, V.; Kukacka, J.; Prusa, R.; Trnkova, L.; Strnadel, J.; Horak, V.; Kizek, R. Effects of reduced glutathione, surface active agents and ionic strength on the detection of metallothioneins by using the Brdicka reaction. Electroanalysis 2009, 21, 640–644. [Google Scholar]
|pH 4||y = 34.478x − 11.073||0.994||5||4.6%||0.10 nM||0.40 nM|
|pH 5||y = 39.723x − 24.233||0.996||5||3.2%||0.01 nM||0.03 nM|
|pH 6||y = 32.108x + 17.833||0.998||5||5.1%||0.25 nM||1.00 nM|
|Sample||Linear model||R2||n||R.S.D (%)||Polynomial model||R2|
|Acetate buffer||y = 39.049x − 20.494||0.9970||5||0.95||y = 0.0298x2 + 36.342x − 4.9257||0.9973|
|Add 10% medium||y = 32.935x + 43.672||0.9892||5||1.35||y = −0.0505x2 + 37.517x + 17.321||0.9903|
|Add 50% medium||y = 20.614x − 0.1286||0.9875||5||1.88||y = −0.0681x2 + 26.797x − 35.691||0.9929|
|Add 80% medium||y = 17.546x + 36.594||0.9882||5||2.49||y = −0.0791x2 + 24.724x − 4.6941||0.9981|
|Add 100% medium||y = 17.663x + 29.924||0.9915||5||3.10||y = −0.0702x2 + 24.04x − 6.7551||0.9993|
R2 confidence coefficient, n number of independent measurements, R.S.D. relative standard deviation (%).
p = 0.05, n = 3.
© 2011 by the authors; licensee MDPI, Basel, Switzerland. This article is an open access article distributed under the terms and conditions of the Creative Commons Attribution license (http://creativecommons.org/licenses/by/3.0/).