- Open Access
Antimicrobial activities of commercial nanoparticles against an environmental soil microbe, Pseudomonas putida KT2440
© Gajjar et al; licensee BioMed Central Ltd. 2009
- Received: 06 February 2009
- Accepted: 26 June 2009
- Published: 26 June 2009
The release of heavy metal-containing nanoparticles (NP) into the environment may be harmful to the efficacy of beneficial microbes that function in element cycling, pollutant degradation and plant growth. Nanoparticles of Ag, CuO and ZnO are of interest as antimicrobials against pathogenic bacteria. We demonstrate here their antimicrobial activity against the beneficial soil microbe, Pseudomonas putida KT2440.
Toxicity was detected in a KT2440 construct possessing a plasmid bearing the luxAB reporter genes. "As manufactured" preparations of nano- Ag, -CuO and -ZnO caused rapid dose-dependent loss of light output in the biosensor. Cell death accompanied loss in Lux activity with treatments by nano-Ag and -CuO, but with -ZnO the treatments were bacteriostatic rather than bactericidal. Bulk equivalents of these products showed no inhibitory activity, indicating that particle size was determinant in activity. Flow Field-Flow Fractionation (FlFFF) of an aqueous suspension of the nano-CuO and ZnO revealed a small proportion of 5 nm NP and aggregated particulates with sizes ranging between 70 nm and 300 nm; the majority portion of material was aggregated into particles larger than 300 nm in size. Thus within the commercial preparation there may be microbially active and inactive forms.
The "as-made" NP of Ag, CuO and ZnO have toxic effects on a beneficial soil microbe, leading to bactericidal or bacteriostatic effects depending on the NP employed. The lack of toxicity from bulk materials suggests that aggregation of the NP into larger particles, possibly by factors present in the environment may reduce their nontarget antimicrobial activity.
- Inductively Couple Plasma Mass Spectrometry
- Light Output
- Biosensor Cell
- KT2440 Cell
- Beneficial Soil Microbe
Nanotechnology has attracted global attention because nanoparticles (NP) have properties unique from their bulk equivalents. NP of Ag, CuO and ZnO are being used industrially for several purposes including amendments to textiles, cosmetics, sprays, plastics and paints . A common feature of these three NP is their antimicrobial activity [2–8]. The antimicrobial activity of NP largely has been studied with human pathogenic bacteria, mainly Escherichia coli and Staphylococcus aureus. Nano-Ag is inhibitory to E. coli [5, 9–16] and S. aureus [5, 9, 12, 16]. These microbes also are sensitive to nano-CuO and nano-ZnO [17, 18].
NP of Ag, CuO and ZnO are reported to attack bacterial membranes. Short exposure of E. coli cells to nano-Ag destabilizes the outer membrane, collapses the plasma membrane potential and decreases ATP . Pits in E. coli cell walls were observed after nano-Ag treatment  and promoted release of green fluorescent protein from transformed E. coli cells . Exposure of E. coli to nano-ZnO also causes loss in membrane integrity . Likewise, toxicity of NP of CuO and ZnO are connected with cell membrane damage .
NP action may be due in part to their release of free ions. Heavy metal ions have diverse effects on bacterial cell function. For Cu ions, the mechanism may involve oxidative stress . The redox cycling of Cu ions results in depletion of glutathione and affects the sulfhydryl groups of proteins causing DNA damage and lipid oxidation . Like Cu, Zn also is an essential element for cells; levels of Zn above the essential threshold level inhibit bacterial enzymes including dehydrogenase  and certain protective enzymes, such as thiolperoxidase, and glutathione reductase . Zn inhibition of NADH oxidase is proposed to impede the respiratory chain of E. coli . Additionally, loss of membrane potential is associated with inhibition by Zn ions at cytochrome c oxidase in Rhodobacter sphaeroides . Ag ions inactivate proteins with SH groups and prevent the ability of DNA to replicate . Holt and Bard  propose that NADH dehydrogenase in the electron transport chain of E coli is inhibited by Ag ions.
Extensive use and increasing demand for NP will lead to their accumulation in the environment, especially in landfills and their water effluents. Control of pathogenic microbes by antimicrobial NP is a promising approach to defeat the multiresistant pathogens such as methicillin-resistant S. aureus . However, nontarget effects on the populations of microbes that play beneficial roles in the environment could have negative consequences. Many microbes have essential roles in element cycling, (carbon, sulfur, nitrogen, etc.), while others degrade pollutants and promote plant growth [25–31]. Nowack and Bucheli  found little published information about the release of NP in the environment in their efforts to model the risk of Ag NP. Novel and unprecedented sources are likely: recently, commercially available nano-Ag-treated socks were found to release Ag upon washing the socks . Concern for nontarget effects of environmental accumulation of Ag has been raised .
The toxicity of NP against environmental microbes has been little studied. Vibrio fisheri has been used because of its natural light emitting property in assessment of toxicity and Bacillus subtilis has been examined as an example of a spore-forming bacterium [4, 5, 17]. The aim of this study was to evaluate the antimicrobial activity of nano-Ag, nano-CuO and nano-ZnO using a biosensor constructed in Pseudomonas putida KT2440. This pseudomonad is beneficial in the environment because of its bioremediation potential and it is a strong root colonizer [25, 35, 36]. The biosensor was constructed to emit light from luxAB genes under the control of a promoter containing a single heavy metal binding domain (MTCGHC). Because the luciferase encoded by luxAB requires FMNH2 as a substrate, expression from this promoter permits light output dependent on the energy status of the cells .
We report on the responses of the biosensor to NP of Ag, CuO and ZnO in comparison with the effects of bulk equivalents and free metal ions. We examined how loss of Lux activity correlated with changes in culturability of the cell as an effort to understand more of the potential environmental impacts of NP, a need discussed by Nowack and Bucheli . We also document the sizes of the NP in aqueous suspension of the nano-metal oxides through the use of Flow Field-Flow Fractionation (FlFFF); aggregation of commercial preparations of NP is commonly reported.
ATTOSTAT (NLC Laboratories, Salt Lake City, UT) was used as the nano-Ag source, with NP of a reported size 10 nm and a concentration of 30 mg Ag/L. The bulk Ag source was from Alfa Aesar, Ward Hill, MA, with a reported particle size of 44,000 nm. Bulk and NP of CuO and ZnO were purchased from Sigma-Aldrich, St. Louis, MO. The reported "as manufactured" sizes were: nano-CuO, 33 nm; nano-ZnO, 50–70 nm; bulk CuO, 8000–9000 nm; and ZnO, less than 1000 nm. Exposure to ions was from solutions of CuCl2, Zn(NO3)2 and AgNO3. All solutions were prepared in distilled, sterile water.
Biosensor construction and use
The biosensor was constructed in strain P. putida KT2440 to harbor a plasmid with a luxAB fusion to a Cu-responsive promoter [Pettee et al., unpublished]. Oligonucleotide primers were designed to amplify approximately 500 bps 5' to 100 bps 3' downstream of the translational start site at locus PP_0588 in wild type P. putida KT2440. The primers were: For, CGATGCGGTATTTGTTGATCT and Rev, AATCGCAGTGAGGATCTGCT. PCR products containing the PP_0588 promoter region were ligated to the promoterless luxAB::npt cassette in plasmid pCR2.1 5' bearing resistance genes for kanamycin and ampicillin (Invitrogen.com) in E. coli. Determination of the promoter orientation in the clones was achieved by PCR analysis using a primer to the 5' end of the luxA gene in the reverse orientation and identifying PCR products when used with the 5' promoter primer of PP_0588, 5'-CGATGCGGTATTTGTTGATCT-3'. The luxA primer sequence was 5'-CAACCAAATTTTCCCCAAGA-3'. Positive clones were ultimately confirmed by the presence of Lux activity and ability to grow on kanamycin at 20 μg/ml. The PP_0588 lux fusion was removed from the pCR2.1 vector and inserted into the stable plasmid pCPP45, bearing a resistance gene for tetracycline, for triparental mating into P. putida KT2440.
The PP_0588 cells were stored in 15% glycerol at -80°C. Logarithmic phase cells were generated by reculturing from an overnight culture grown in minimal medium (MM) with shaking at 25°C to OD600nm = 0.1. MM contained in 1 L: 10.5 g K2HPO4, 4.5 g KH2PO4, 0.5 g sodium citrate (2H2O), 1.0 g (NH4)2 SO4, 0.25 g MgSO4.7H2O, and 2.0 g sucrose. The culture (200 ml) was centrifuged at 10,000 g for 10 min and the cells were resuspended in 200 ml sterile distilled water and used immediately in the Lux assay. After dividing into 50 ml aliquots in 125 ml flasks, the suspensions were treated with NP, bulk material or ions at defined final concentrations or were left without treatment as a control. Initially the cells were treated with 0.1, 1 and 10 mg metal (M)/L to determine the sensitivity range. Subsequently doses were adjusted to determine the level at which toxicity was observed. Flasks were shaken at 200 rpm and 25°C during the study. At defined times, 200 μl of the suspensions were transferred in triplicate into well plates for Lux readings. The luciferase substrate, 1% decanal in ethanol, 10 μl, was added automatically in the L MAXII Luminometer (Molecular Devices Corporation, Sunnyvale CA). Light output was recorded with a 10 sec. exposure. Generally samples were assayed every 10 minutes up to 1 h. At each sampling time, the Lux activity from three aliquots of the cell suspension was measured. Each treatment was replicated in three or more separate studies.
Assessment of culturability
Cells, after a 60 minute treatment with or without metal exposure, were assayed for culturability by dilution plating on salt-free Luria Broth (Difco, Sparks, MD) agar medium. Colonies were counted after 24 h incubation at 28°C and the colony forming units (Cfu)/ml determined.
Fractionation of nano-metal oxide particles
An aqueous suspension of 10,000 mg Cu/L of nano-CuO or nano-ZnO in sterile distilled water was filtered sequentially through sterile filters with pore sizes of 450 and 200 nm (Whatman Inc., Florham Park, NJ, USA). The filtrates were collected and diluted 5, 10, 100 or 1000-fold into cultures of KT2440 to determine effect on light output as described above. After 60 minutes of exposure cells were plated to determine culturability.
Flow Field-Flow Fractionation (FlFFF) and ICP-MS analysis
Operation conditions for separation of particles of different size by FlFF
Operating conditions for particles 10–250 nm
Elution time min
Operating conditions for particles less than 10 nm
Elution time min
Description of operational conditions for ICP-MS of fractionated materials.
RF power (W)
Plasma gas flow rate (L/min)
Hydrogen flow rate (mL/min)
Helium flow rate (mL/min)
Carrier flow rate (L/min)
Make-up gas (L/min)
Auxiliary gas (L/min)
Sample flow rate (mL/min)
Acquisition time per isotope (sec)
Total acquisition time for 19 isotopes (sec)
Total running time (sec)
Sample nebulizer tubing:
Internal diameter (mm)
AF4 carrier tubing:
Internal diameter (mm)
Exposure to nano-Ag, bulk-Ag and Ag ions
The tables adjacent to the RLU graphs report the changes in culturability of the cells transferred to plating medium after 60 minutes of treatment compared with unchallenged controls. For treatment with nano-Ag and Ag ions, loss of Lux activity correlated with loss in culturability. No loss in Lux output or culturability was observed with exposure to bulk Ag. At 0.25 mg/L nano-Ag no culturable cells were obtained; with Ag ion a culturability threshold near 0.2 mg Ag ion/L (data not shown) was determined.
Exposure to nano-CuO, bulk-CuO and Cu ions
Loss in Lux correlated with loss in culturability upon exposure to Cu ions and reduced culturability upon exposure to nano-CuO at 10 mg/L treatment. Cell culturability did not decline with bulk CuO exposure.
Exposure to nano-ZnO, bulk-ZnO and Zn ions
None of the treatments with Zn caused complete loss in culturability, rather they were bacteriostatic. Cells grew from the Zn-exposed samples at a delayed rate. Whereas colonies from the control cells could be counted in 2 days, those from cells exposed to zinc required at least 5 days. The culturability data shown in Fig. 3 are after 1 week of growth.
Exposure to mixtures of nanoparticles
Size determination of particles in aqueous suspensions of nano-CuO and nano-ZnO
Biosensor response to filtrates containing 5–200 nm particles from nano-CuO
Treatment of the biosensor cells with the filtrates passing through both 450 nm and 200 nm filters from a suspension of nano-CuO at 10,000 mg Cu/L caused dose dependent loss in light output. No toxicity was observed with a 100-fold dilution of the filtrate but no light was emitted when cells were treated with the × 10 diluted filtrate. The loss in Lux activity with the 10-fold diluted filtrate correlated with loss in culturability. Similarly, treatment with the filtrate prepared from 10,000 mg Zn/L from nano-ZnO at × 5 and × 10, but not × 100 dilution, caused partial loss in light output. In contrast to the filtrate from the nano-CuO, no change in culturability was observed for nano-ZnO (data not shown).
The biosensor constructed in the environmental isolate P. putida KT2440 effectively and rapidly, within minutes, demonstrated dose-dependent toxicity of NP of Ag, CuO and ZnO. These findings illustrate that the toxicity was not restricted to bacteria with pathogenic potential. Rather an environmental isolate, studied because of its bioremediation potential, was affected. The NP of Ag, CuO and ZnO were more toxic, causing loss of Lux activity in the biosensor, than their equivalent bulk materials indicating that the nano-size of the material was important. The findings that nano-Ag, nano-CuO and nano-ZnO reduced Lux activity were consistent with the observations by other groups that these NP caused bacterial membrane damage [6, 10, 13]. We speculate that such damage altered the membrane potential of the cell and, we presume, the availability of the FMNH2 required for the Lux activity. Consequently, Lux activity declined in the biosensor cells.
With Ag, the toxic doses of the NP and the ion were similar (~0.2 mg Ag/L) in the KT2440 cells. For Cu, complete loss of light output required exposure to 10 mg Cu/L from nano-CuO compared with 1.0 mg Cu/L of the Cu ions. Similarly, 7–10 mg Zn/L was required for toxicity of nano-ZnO compared to about a ten fold lower dose of Zn ions. Using nano-CuO and nano-ZnO from sources different from our own, nano-ZnO was more toxic than nano-CuO for Vibrio fischeri , compared with similar toxicity with for KT2440. Combinations of nano-Ag and nano-ZnO or nano-CuO and nano-ZnO were not interactive. However, the combination of nano-Ag plus nano-CuO was more inhibitory than their effects alone and the decrease in Lux correlated with reduction in culturability. These findings suggest that the target sites for nano-Ag and nano-CuO differed.
Toxicity as assessed with the pseudomonad biosensor was at lower NP levels than observed in other assays where culturability on solid or liquid media was the bioassay. For instance, in assays in rich medium, nano-ZnO toxicity required 126 mg Zn/L with S. aureus  and for E. coli and B. subtilis 70 mg/L for nano-Ag  compared with 7–10 mg Zn/L from nano-ZnO and 0.3 mg Ag/L for the pseudomonad. The KT2440 bioassays were performed under conditions with no other added metal ions, thus, limiting possible competition with the heavy metal for bacterial binding sites. Likewise, the inorganic and organic materials that compose most bacterial growth media were not present. Such materials might otherwise complex the metals and change bioavailability.
Size and, thus, aggregation of the NP are important in nanotoxicity. For nano-ZnO, particles of 8 nm in size were more toxic to S. aureus than those that were reported to be larger (50–70 nm); these latter products were from the same Sigma-Aldrich source that we used . Thus, it is interesting that we observed by FlFFF that 5 nm NP were present in the nano-CuO and-ZnO preparations. Exposing the biosensor to filtrates of nano-CuO and ZnO that would contain such particles showed dose dependent effects on light output and cell culturability. The FlFFF fractograms also showed that the aqueous NP suspensions prepared from manufactured NP powders were aggregated into poly-dispersed particulates ranging in size range from 70 nm to larger than 300 nm, with the majority of the Cu and Zn mass being associated with the larger particles.
Unlike the treatments with Cu or Ag, nonlethal doses of zinc from bulk, nano-ZnO and the ion increased light output above the control in the bioassays. To explore whether this was due to Zn activation of the promoter of the PP_0588 locus, we added zinc to a biosensor prepared with the fusion of the same luxAB-npt cassette to the promoter of the pseudomonad catalase gene. No increase in light output was observed with addition of Zn in this construct where the promoter region lacked a metal-sensitive motif (data not shown). These findings suggest that increased Lux activity with the KT2440 biosensor by Zn was promoter-driven, in agreement with the existence of a heavy metal-sensitive element in the promoter of the PP_0588 used in biosensor construct. Also, in the biosensor KT2240 strain we observed zinc caused bacteriostasis. Two other studies report that nano-ZnO was bacteriostatic to Streptococcus and Staphylococcus isolates in both broth medium or on solid agar plates [18, 42]. Additionally the antimicrobial effect of nano-ZnO was reported to be sensitive to activation by the UV-radiation from laboratory lighting , conditions under which our assays were performed. Other studies on toxicity of nano-ZnO to mammalian cells found that solubilization of nano-ZnO as well as release of Zn ions from the NP contributed to activity .
Our observations confirmed that the biosensor generated with Lux as the output signal was a sentinel for cellular toxicity. Similar bacterially-based biosensors have been used previously to examine the toxicity of Cu and Zn in sludges . Collectively, our findings show that NP preparations containing the heavy metals Ag, Cu and Zn were toxic to the beneficial environmental microbe, P. putida KT2440, suggesting that the NP at certain concentrations (≤ 1 mg Ag/L, ≈ 10 mg Cu, Zn/L) can be an environmental risk. The impact of the nano-metal oxides on cell culturability was dependent on the chemistry of the particles, with Zn causing bacteriostasis whereas Cu and Ag were bactericidal. FlFFF of the aqueous suspensions of the nano-metal oxides showed most of the mass was in aggregates greater than 300 nm although these ranged downward with another peak at 5 nm. Our findings suggest that further studies on determining the factors that affect aggregation of commercial NP in the environment are required. It is likely that such aggregation would reduce the deleterious effect of as-made NP on nontarget microbes. Implementing conditions promoting NP aggregation could alleviate point-source contamination.
We thank Dr. CD Miller and Chun Zhang MS for providing the biosensor construct. AJA acknowledges the EPA for a STAR-grant on risk assessment of heavy metals that initiated the construction of the biosensor. DWB and AJA thank the Utah Agricultural Experiment Station for support. DWB, AJA, and WPJ gratefully acknowledge support from USDA-CSREES grant 2009-35603-05037. AES Experimental Journal Paper Number 8008.
- Mueller NC, Nowack B: Exposure modeling of engineered nanoparticles in the environment. Environ Sci Technol 2008,42(12):4447-4453. 10.1021/es7029637View ArticleGoogle Scholar
- Blaser SA, Scheringer M, Macleod M, Hungerbühler K: Estimation of cumulative aquatic exposure and risk due to silver: contribution of nano-functionalized plastics and textiles. Sci Total Environ 2008,390(2–3):396-409.View ArticleGoogle Scholar
- AmericanElements: Silver Nanoparticles.2007. [http://www.americanelements.com/agnp.html]Google Scholar
- Adams LK, Lyon DY, Alvarez PJ: Comparative eco-toxicity of nanoscale TiO 2 , SiO 2 and ZnO water suspensions. Water Res 2006,40(19):3527-3532. 10.1016/j.watres.2006.08.004View ArticleGoogle Scholar
- Yoon KY, Hoon Byeon J, Park JH, Hwang J: Susceptibility constants of Escherichia coli and Bacillus subtilis to silver and copper nanoparticles. Sci Total Environ 2007,373(2–3):572-575.View ArticleGoogle Scholar
- Reddy KM, Feris K, Bell J, Wingett DG, Hanley C, Punnoose A: Selective toxicity of zinc oxide nanoparticles to prokaryotic and eukaryotic systems. Appl Phys Lett 2007,90(213902):2139021-2139023.Google Scholar
- Stohs SJ, Bagchi D: Oxidative mechanisms in the toxicity of metal ions. Radic Biol Med. 1995,18(2):321-336. 10.1016/0891-5849(94)00159-HView ArticleGoogle Scholar
- Cioffi N, Torsi L, Ditaranto N, Tantillo G, Ghibelli L, Sabbatini L, Bleve-Zacheo T, D'Alessio M, Zambonin PG, Traversa E: Copper nanoparticle/polymer composites with antifungal and bacteriostatic properties. Chem Mater 2005, 17: 5255-5262. 10.1021/cm0505244View ArticleGoogle Scholar
- Kim JS, Kuk E, Yu KN, Kim JH, Park SJ, Lee HJ, Kim SH, Park YK, Park YH, Hwang CY, Kim YK, Lee YS, Jeong DH, Cho MH: Antimicrobial effects of silver nanoparticles. Nanomedicine 2007,3(1):95-101.View ArticleGoogle Scholar
- Lok CN, Ho CM, Chen R, He QY, Yu WY, Sun H, Tam PK, Chiu JF, Che CM: Proteomic analysis of the mode of antibacterial action of silver nanoparticles. J Proteome Res 2006,5(4):916-924. 10.1021/pr0504079View ArticleGoogle Scholar
- Pal S, Tak YK, Song JML: Does the antibacterial activity of silver nanoparticles depend on the shape of the nanoparticle? A study of the Gram-negative bacterium Escherichia coli . Appl Environ Microbiol 2007,73(6):1712-1720. 10.1128/AEM.02218-06View ArticleGoogle Scholar
- Shahverdi AR, Fakhimi A, Shahverdi HR, Minaian S: Synthesis and effect of silver nanoparticles on the antibacterial activity of different antibiotics against Staphylococcus aureus and Escherichia coli . Nanomedicine 2007,3(2):168-171.View ArticleGoogle Scholar
- Sondi I, Salopek-Sondi B: Silver nanoparticles as antimicrobial agent: a case study on Escherischia coli as a model for Gram-negative bacteria. J Colloid Interface Sci 2004,275(1):177-182. 10.1016/j.jcis.2004.02.012View ArticleGoogle Scholar
- Gogoi SK, Gopinath P, Paul A, Ramesh A, Ghosh SS, Chattopadhyay A: Green fluorescent protein-expressing Escherichia coli as a model system for investigating the antimicrobial activities of silver nanoparticles. Langmuir 2006,22(22):9322-9328. 10.1021/la060661vView ArticleGoogle Scholar
- Panacek A, Kvítek L, Prucek R, Kolar M, Vecerova R, Pizùrova N, Sharma VK, Nevecna T, Zboril R: Silver colloid nanoparticles: synthesis, characterization, and their antibacterial activity. J Phys Chem B 2006,110(33):16248-16253. 10.1021/jp063826hView ArticleGoogle Scholar
- Ruparelia JP, Chatterjee AK, Duttagupta SP, Mukherji S: Strain specificity in antimicrobial activity of silver and copper nanoparticles. Acta Biomater. 2008,4(3):707-716. 10.1016/j.actbio.2007.11.006View ArticleGoogle Scholar
- Heinlaan M, Ivask A, Blinova I, Dubourguier HC, Kahru A: Toxicity of nanosized and bulk ZnO, CuO and TiO(2) to bacteria Vibrio fischeri and crustaceans Daphnia magna and Thamnocephalus platyurus . Chemosphere 2008,71(7):1308-1316. 10.1016/j.chemosphere.2007.11.047View ArticleGoogle Scholar
- Jones N, Ray B, Ranjit KT, Manna AC: Antibacterial activity of ZnO nanoparticle suspensions on a broad spectrum of microorganisms. FEMS Microbiol Lett 2008,279(1):71-76. 10.1111/j.1574-6968.2007.01012.xView ArticleGoogle Scholar
- Nweke CO, Alisi CS, Okolo JC, Nwanyanwu CE: Toxicity of Zinc to heterotrophic bacteria from a tropical river sediment. Applied Ecology and Environmental Research 2007,5(1):123-132.View ArticleGoogle Scholar
- Nguyen TMP, Phan TN, Robert EM: Zinc effects on oxidative physiology of oral bacteria. Advances in Natural Sciences 2006, 7: 131-138.Google Scholar
- Beard SJ, Hughes MN, Poole RK: Inhibition of the cytochrome bd-terminated NADH oxidase system in Escherichia coli K-12 by divalent metal cations. FEMS Microbiol Lett 1995,131(2):205-210. 10.1111/j.1574-6968.1995.tb07778.xView ArticleGoogle Scholar
- Mills DA, Schmidt B, Hiser C, Westley E, Ferguson-Miller S: Membrane potential-controlled inhibition of cytochrome c oxidase by zinc. J Biol Chem 2002,277(17):14894-14901.Google Scholar
- Feng QL, Wu J, Chen GQ, Cui FZ, Kim TN, Kim JO: A mechanistic study of the antibacterial effect of silver ions on Escherichia coli and Staphylococcus aureus . J Biomed Mater Res 2000,52(4):662-668. 10.1002/1097-4636(20001215)52:4<662::AID-JBM10>3.0.CO;2-3View ArticleGoogle Scholar
- Holt KB, Bard AJ: Interaction of silver (I) ions with the respiratory chain of Escherichia coli : an electrochemical and scanning electrochemical microscopy study of the antimicrobial mechanism of micromolar. Biochemistry. 2005,44(39):13214-13223. 10.1021/bi0508542View ArticleGoogle Scholar
- Molina MA, Ramos JL, Espinosa-Urgel M: A two-partner secretion system is involved in seed and root colonization and iron uptake by Pseudomonas putida KT2440. Environ Microbiol 2006,8(4):639-647. 10.1111/j.1462-2920.2005.00940.xView ArticleGoogle Scholar
- Osler GH, Sommerkorn M: Toward a complete soil C and N cycle: incorporating the soil fauna. Ecology 2007,88(7):1611-1621. 10.1890/06-1357.1View ArticleGoogle Scholar
- Kertesz MA, Mirleau P: The role of soil microbes in plant sulphur nutrition. J Exp Bot 2004,55(404):1939-1945. 10.1093/jxb/erh176View ArticleGoogle Scholar
- Khan AG: Role of soil microbes in the rhizospheres of plants growing on trace metal contaminated soils in phytoremediation. J Trace Elem Med Biol 2005,18(4):355-364. 10.1016/j.jtemb.2005.02.006View ArticleGoogle Scholar
- Gupta A, Gopal M, Tilak KV: Mechanism of plant growth promotion by rhizobacteria. Indian J Exp Biol 2000,38(9):856-862.Google Scholar
- Dos Santos VA, Heim S, Moore ER, Strätz M, Timmis KN: Insights into the genomic basis of niche specificity of Pseudomonas putida KT2440. Environ Microbiol 2004,6(12):1264-1286. 10.1111/j.1462-2920.2004.00734.xView ArticleGoogle Scholar
- Van Wees SC, Ent S, Pieterse CM: Plant immune responses triggered by beneficial microbes. Curr Opin Plant Biol 2008,11(4):443-448. 10.1016/j.pbi.2008.05.005View ArticleGoogle Scholar
- Nowack B, Bucheli TD: Occurrence, behavior and effects of nanoparticles in the environment. Environ Pollut 2007,150(1):5-22. 10.1016/j.envpol.2007.06.006View ArticleGoogle Scholar
- Benn TM, Westerhoff P: Nanoparticle silver released into water from commercially available sock fabrics. Environ Sci Technol 2008,42(11):4133-4139. 10.1021/es7032718View ArticleGoogle Scholar
- Eckelman MJ, Graedel TE: Silver emissions and their environmental impacts: a multilevel assessment. Environ Sci Technol 2007,41(17):6283-6289. 10.1021/es062970dView ArticleGoogle Scholar
- Ramos-González MI, Campos MJ, Ramos JL: Analysis of Pseudomonas putida KT2440 gene expression in the maize rhizosphere: in vivo expression technology capture and identification of root-activated promoters. J Bacteriol 2005,187(12):4033-4041. 10.1128/JB.187.12.4033-4041.2005View ArticleGoogle Scholar
- Child R, Miller CD, Liang Y, Narasimham G, Chatterton J, Harrison P, Sims RC, Britt D, Anderson AJ: Polycyclic aromatic hydrocarbon-degrading Mycobacterium isolates: their association with plant roots. Appl Microbiol Biotechnol 2007,75(3):655-663. 10.1007/s00253-007-0840-0View ArticleGoogle Scholar
- Koga K, Harada T, Shimizu H, Tanaka K: Bacteria luciferase activity and the intracellular redox pool in Escherichia coli . Mol Genet Genomics 2005,274(2):180-188. 10.1007/s00438-005-0008-5View ArticleGoogle Scholar
- Giddings JC: Field-flow fractionation. Separ Sci Technol 1985,19(11&12):831-847.Google Scholar
- Giddings JC: Field-flow fractionation: Analysis of macromolecular, colloidal and particulate materials. Science 1993,260(5113):1456-1465. 10.1126/science.8502990View ArticleGoogle Scholar
- Prestel H, Schott L, Niessner R, Panne U: Characterization of sewage plant hydrocolloids using asymmetrical flow field-flow fractionation and ICP-mass spectrometry. Water Res 2005,39(15):3541-3552. 10.1016/j.watres.2005.06.027View ArticleGoogle Scholar
- Litzén A: Separation speed, retention, and dispersion in asymmetrical flow field-flow fractionation as functions of channel dimensions and flow rates. Analytical Chemistry 1993,65(5):461-470. 10.1021/ac00052a025View ArticleGoogle Scholar
- Huang Z, Zheng X, Yan D, Yin G, Liao X, Kang Y, Yao Y, Huang D, Hao B: Toxicological effect of ZnO nanoparticles based on bacteria. Langmuir 2008,24(8):4140-4144. 10.1021/la7035949View ArticleGoogle Scholar
- Xia T, Kovochich M, Liong M, Mädler L, Gilbert B, Shi H, Yeh JI, Zink JI, Nel AE: Comparison of the mechanism of toxicity of zinc oxide and cerium oxide nanoparticles based on dissolution and oxidative stress properties. ACS Nano 2008, 2: 2121-2134. 10.1021/nn800511kView ArticleGoogle Scholar
- Chaudri AM, Lawlor K, Preston S, Paton GI, Kikkham K, McGrath SP: Response of a Rhizobium-based luminescence biosensor to Zn and Cu in soil solutions from sewage sludge treated soils. Soil Biology and Biochemistry 2000, 32: 383-388. 10.1016/S0038-0717(99)00166-2View ArticleGoogle Scholar
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