To provide a basis for using indigenous bacteria for bioremediation of heavy metal contaminated soil, the heavy metal resistance and plant growth-promoting activity of 136 isolates from V-Ti magnetite mine tailing soil were systematically analyzed. Among the 13 identified bacterial genera, the most abundant genus was Bacillus (79 isolates) out of which 32 represented B. subtilis and 14 B. pumilus, followed by Rhizobium sp. (29 isolates) and Ochrobactrum intermedium (13 isolates). Altogether 93 isolates tolerated the highest concentration (1000 mg kg−1) of at least one of the six tested heavy metals. Five strains were tolerant against all the tested heavy metals, 71 strains tolerated 1,000 mg kg−1 cadmium whereas only one strain tolerated 1,000 mg kg−1 cobalt. Altogether 67% of the bacteria produced indoleacetic acid (IAA), a plant growth-promoting phytohormone. The concentration of IAA produced by 53 isolates was higher than 20 µg ml−1. In total 21% of the bacteria produced siderophore (5.50–167.67 µg ml−1) with two Bacillus sp. producing more than 100 µg ml−1. Eighteen isolates produced both IAA and siderophore. The results suggested that the indigenous bacteria in the soil have beneficial characteristics for remediating the contaminated mine tailing soil.
Citation: Yu X, Li Y, Zhang C, Liu H, Liu J, Zheng W, et al. (2014) Culturable Heavy Metal-Resistant and Plant Growth Promoting Bacteria in V-Ti Magnetite Mine Tailing Soil from Panzhihua, China. PLoS ONE 9(9): e106618. https://doi.org/10.1371/journal.pone.0106618
Editor: Andrew C. Singer, NERC Centre for Ecology & Hydrology, United Kingdom
Received: May 14, 2014; Accepted: July 29, 2014; Published: September 4, 2014
Copyright: © 2014 Yu et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: The authors confirm that all data underlying the findings are fully available without restriction. All relevant data are within the paper and its Supporting Information files.
Funding: This work was financially supported by National Natural Science Foundation of China (NO. 31300461), Doctoral Fund of Ministry of Education of China (NO. 20135103120003), and Research Foundation for the Introduction of Talent of Sichuan Agricultural University. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Mining industry has caused extensive environmental and public health problems –. A wide variety of heavy metals such as zinc, lead, copper and cadmium have been detected in soil at mining sites presenting a major threat to the environment and population , . Heavy metals cannot be biologically degraded and indefinitely persist in the environment. Heavy metals transferred through the food chain are a serious hazard to human health . Due to contamination by heavy metals, mining sites are surrounded by large barren areas. The awareness of the detrimental heavy metal contamination at mining sites has increased in recent years.
The toxic heavy metals accumulated in soil can effectively impact the microbial community composition. Bacteria play an important role in maintaining soil fertility and structure. Because bacteria respond quickly and are sensitive to subtle environmental changes, they have been considered as efficient bio-indicators of soil quality . Both the structural and functional bacterial diversity are important indicators of soil health . Phytoremediation has been effectively used to remediate heavy metal-polluted sites as a sustainable remediation approach . Plant-microbe partnerships may be utilized to improve biomass production and remediation . Plant growth-promoting rhizobacteria (PGPR) that solubilize phosphate and synthesize growth-promoting substances such as indoleacetic acid (IAA) and siderophores can be applied in the plant-assisted bioremediation of metal-contaminated soil –. Phytoremediation utilizes heavy metal-tolerant plant species with metal accumulation ability. Since the addition of IAA to soil can enhance the uptake of metals in plant roots , , bacteria-producing IAA have been used to assist the phytoremediation of soil contaminated with heavy metals .
Metals such as iron, zinc, copper, manganese and nickel play important roles as essential or beneficial micronutrients of microorganisms , . However, a high concentration of metal ions in soil shows serious effects on microbial communities by changing the community structure and decreasing diversity and total microbial biomass . Therefore, microbial communities are useful indicators of the effect of contamination on soil health . To have a functional role in remediation, bacteria in heavy metal-contaminated soil must first overcome the heavy metal stress. Microorganisms tolerate heavy metals by immobilizing metals on cell surfaces or transforming metals into less toxic forms, for example by precipitation, acidification and oxidation-reduction .
Panzhihua is an industrial and mining city in Sichuan of Southwest China with over 109 tonnes of ore reserves deposited as iron-vanadium-titanium oxide (V-Ti magnetite) . The world class magmatic deposits of V-Ti magnetite in Panzhihua provide 20% of iron (Fe), 64% of vanadium (V) and 53% of titanium (Ti) supply for China . Long-term mining activities have contaminated soils and sediments in Panzhihua by metals, especially by V, Ti and Fe . The redox-sensitive vanadium is toxic to soil microorganisms and plants . Even though titanium is beneficial to plants at low concentrations, high concentrations of titanium are toxic . Iron is an essential nutrient serving as a catalyst for many cellular reactions, in particular those involving redox and O2 chemistry . More than 220 million m3 of mine tailing has been piled up in Zhujiabaobao, Panzhihua, creating a serious environmental hazard. Because the mine tailing soil contains heavy metals, only few plants grow on it, creating large barren areas. Long term exposure to contaminant allows different bacteria to become adapted to the contaminant, making autochthonous bacteria more useful in bioremediating the contaminated environment compared to allochthonous ones . Therefore, this study focuses on the culturable heavy metal-resistant and plant growth-promoting autochthonous bacteria from V-Ti magnetite mine tailing soil, with the aim of providing information for bioremediating the large area covered by the V-Ti magnetite mine tailing dam at Panzhihua.
Materials and Methods
Study site and soil sampling
Panzhihua (N26°05′∼27°21′, E101°08′∼102°15′) in Sichuan, China, is an important industrial and mining base with abundant mineral resources. Panzhihua V-Ti magnetite mine is by the Jinsha River in the southern part of Panxi rift valley upstream of the Yangtze River. The mining area includes six large scale iron deposits, numerous medium-sized coal, clay, dolomite and limestone deposits, and minor graphite, manganese and barite deposits . Our study site did not involve endangered or protected species and provide a specific location, so no specific permissions were required for the location/activity.
Zhujiabaobao (N 26°37′2″, E 101°45′56″) in Panzhihua is a huge deposit of V-Ti magnetite. In the Zhujiabaobao mining area, there is more than 220 million m3 of mine tailing and a large tailing dam. The ground around the tailing dam is barren and desert-like. Four soil samples were collected in May 2013 to a depth of 0–20 cm from the tailing dam by a five-point sampling method. Soil samples, fully mixed in sterile polyethylene bags, were kept at room temperature in the dark.
Chemical analyses of soil samples
The soil samples were dispersed and passed through a 2 mm sieve before measuring pH, organic matter content and the concentrations of available nitrogen (N), phosphorus (P) and potassium (K) as described . Soil available N was determined by Aalkali N-proliferation method, whereas and available P and K quantified with the ASI method. Soil organic matter was determined by the K2CrO7−H2SO4 oxidation method. To extract heavy metals, air-dried soil samples were passed through a 2 mm nylon sieve, and digested by 1∶2∶2 (V:V:V) HNO3:HCl:HClO4. Vanadium (V), titanium (Ti), iron (Fe), nickel (Ni), lead (Pb), zinc (Zn), manganese (Mn), copper (Cu), arsenic (As), cadmium (Cd) and chromium (Cr) were measured by inductively coupled plasma atomic emission spectroscopy (ICP-AES, IRIS Intrepid II, Thermo Electron corporation, USA) as described .
Isolation of bacteria
A sample of 5 grams of soil was suspended in 45 ml sterile water with glass beads. After shaking for 30 minutes and letting settle for 5 minutes, 200 µl of the liquid phase was inoculated on beef extract-peptone agar medium (beef extract 3.0 g l−1, peptone 10.0 g l−1, NaCl 5.0 g l−1, agar 18.0 g l−1, pH 7.0) in Petri dish (90 mm diameter×10 mm depth). Isolates were selected based on differences in colony morphology and re-streaked several times on beef extract-peptone agar at 28°C until 136 pure cultures were obtained.
Genetic identification of isolated bacteria
Total DNA was extracted by the phenol-chloroform method as described . To group the 136 isolates, BOX-PCR with the primer BOXA1R (5′-CTACGGCAAGGCGACGCTGACG-3′) was carried out as described , . A dendrogram based on the BOXA1R-PCR fingerprints was drawn using Numerical Taxonomy and Multivariate Analysis System NTSYSpc 2.2 (Exeter Software, USA). An isolate from each of the 91 BOXA1R-PCR groups was chosen for 16S rRNA gene sequencing. Almost full length 16S rRNA gene was amplified by polymerase chain reaction (PCR) with the universal primers of 27F (5′-AGAGTTTGATCCTGGCTCAG-3′) and 1492R (5′-GGTTACCTTGTTACGACTT-3′) ,  and sequenced at the Beijing Genomics Institute (Shenzhen, China). The sequences were submitted GenBank to assign accession numbers. The closest matching sequences were searched from GenBank with BLAST . A neighbor joining the 16S rRNA phylogenetic tree was constructed using the neighbor joining method in MEGA 6.0 .
Heavy metal tolerance tests
The resistance of the 136 isolates to lead, cadmium, zinc, copper, cobalt and nickel was assayed by spot-inoculating 10 µl of 108 cells ml−1 bacterial suspension on beef extract-peptone agar medium with the respective metal salts. Pb(NO3)2, CdCl2, ZnCl2, CuSO4, CoCl2 and NiCl2 were added to the medium to obtain 200, 400, 600, 800 and 1000 mg kg−1 heavy metal concentrations. After incubation at 28°C for 5 days, the minimum inhibitory concentration (MIC) was defined as the lowest concentration of metal salt inhibiting bacterial growth. On the positive control plates without heavy metal the colonies were approximately four mm in diameter.
Indoleacetic acid and siderophore production assays
The plant growth-promoting activity of the isolates was evaluated by assaying the production of indole-3-acetic acid (IAA) and siderophores as described. In the qualitative IAA assay , isolates were grown in a beef extract-peptone liquid medium with 0.5 g l−1 tryptophan at 28°C and 140 rpm for 36 hours, 50 µl of the culture suspension was absorbed into a white porcelain board and, after adding 100 µl of the color reagent (4.5 g l−1 FeCl3, 57.6% H2SO4), the board was incubated at 25°C for 30 min. A pink color indicated positive IAA production. A non-inoculated beef extract-peptone liquid medium with tryptophan served as a negative control. To quantify IAA production , , 4 ml of the color reagent was added to 2 ml of the culture supernatant obtained by centrifugation (8000 rpm for 5 min). Optical density at 550 nm was measured by spectrophotometry (WFJ2100, UNICO, China) after coloration for 30 min. IAA concentration in the supernatant was interpolated using an IAA standard curve. The distribution of IAA producers and heavy metal tolerant strains among the different taxa were compared with a Chi-square test.
In the qualitative siderophore assay, isolates were grown on chrome azurol sulphonate (CAS) agar to select siderophore producing strains . To quantify siderophore production, siderophore producing strains were grown in Fiss minimal medium (5.03 g l−1 L-asparagine, 5.03 g l−1 KH2PO4, 5.0 g l−1 glucose, 0.5 mg l−1 ZnCl2, 40 mg l−1 MgSO4 and 0.5 µM FeSO4) for two days. After centrifugation at 1000 g for 15 min, supernatant was mixed with CAS solution (1 vol: 1 vol) and incubated for 60 min. Optical density at 400 nm was measured by spectrophotometry (WFJ2100, UNICO, China) . Siderophore concentration in the supernatant was interpolated using a deferoxamine mesylate salt (SIGMA, USA) standard curve. The IAA and siderophore production and heavy metal tolerance assays were done in triplicate.
Basic physicochemical properties of soil samples
To assess the quality of the V-Ti magnetite mine tailing soil, we first measured the soil physicochemical characteristics and heavy metal content in the soil (Table 1). The soil pH was low (5.28±0.91), as was the content of organic matter (16.98±4.45‰). Of the 103.50±36.84 mg kg−1 total N, approximately 13% was plant-available N. As expected, the iron, titanium and vanadium concentrations were high, up to 76.15, 28.19 and 5.58 g kg−1, respectively. The manganese concentration was 1.42 g kg−1. The concentration of chromium, zinc, copper and nickel were 98.51, 87.72, 56.75 and 48.11 mg kg−1. In addition, lead (3.87 mg kg−1), arsenic (0.94 mg kg−1) and Cadmium (0.52±0.25 mg kg−1) were detected in the mine tailing soil.
Isolation of bacteria and genetic identification
Based on differences in colony morphology, 136 bacterial strains were isolated from the V-Ti magnetite mine tailing soil. According to the BOX A1R-PCR fingerprint analysis, the similarities between the 136 isolates ranged from 0.54 to 1.00. Altogether there were 91 distinct fingerprint patterns. The 136 isolates were divided into two major groups, group I (81 isolates) and group II (55 isolates), at 54% similarity level (Figure S1). One strain was chosen from each of the 91 distinct fingerprint pattern groups for 16S rRNA sequencing (Figure S1). The sequences were assigned GenBank accession numbers KJ733935–KJ734025 (Table S1). The16S rRNA gene sequences of the 91 representative strains indicated that the group I and group II in the BOX A1R-PCR dendrogram represented Gram-positive and Gram-negative bacteria, respectively (Table S1, Figure S1). Seventy-nine isolates belonged to the genus Bacillus and represented eleven species (Table S1). Altogether 32 isolates were considered as representing B. subtilis and 14 as B. pumilus (Figure 1, Table S1). In addition to the Bacillus spp. isolates, isolates KT19 and KT84 were identified as Gram-positive strains displaying 99% similarity to the type strains of Paenibacillus tundrae and Microbacterium aerolatum, respectively (Figure 1, Table S1).
The scale bar corresponds to 0.05 substitutions per nucleotide position. The numbers at nodes indicated the levels of bootstrap support (%) based on 1,000 resampled data sets; only values above 50% are given. Superscript “T” means type stains; Number in parentheses represents the sequence number in GenBank. Nanoarchaeum equitans Kin4-M was used as an outgroup.
The 55 Gram-negative isolates were assigned to seven families and ten genera (Figure 1, Table S1). Altogether 43 of them belonged to the Rhizobiaceae and were assigned as Rhizobium sp. (29 isolates), Ochrobactrum intermedium (13 isolates) and Sinorhizobium adhaerens (1 isolate).
Heavy metal tolerance of isolated bacteria
The heavy metal tolerance of the 136 bacterial isolates from the V-Ti magnetite mine tailing soil was determined as the minimum inhibitory concentration (MIC) (Figure 2). Most isolates showed MIC lower than 200 mg kg−1 for Zn (68.4%), Co (87.5%) and Ni (74.3%). Altogether 93 isolates tolerated the highest concentration (1,000 mg kg−1) of at least one tested heavy metal; 71 strains tolerated 1,000 mg kg−1 cadmium whereas only one strain, Bacillus sp. KT-76, tolerated 1,000 mg kg−1 cobalt. Only three strains, the Rhizobium sp. KT27 and KT62, and the Bacillus sp. KT43 displayed MIC less than 200 mg kg−1 for all the six heavy metals tested. Five strains, the B. licheniformis KT-87 and KT-88 and the Bacillus sp. KT-72, KT-74 and KT-76 were tolerant against all the tested heavy metals. B. licheniformis KT87 showed 1000 mg kg−1 MIC for Cd, Zn, Cu and Ni, 800 mg kg−1 MIC for Pb and 600 mg kg−1 MIC for Co. The MIC of Bacillus sp. KT72 for the six heavy metals was 1000 mg kg−1 (Pb, Cd, Ni) and 600 mg kg−1 (Zn, Cu, Co). When comparing the percentage of strains tolerant to four or more heavy metals, it was noted that, among the Rhizobium sp., multiple tolerant strains (34.9%) were less abundant than among the Bacillus spp. (54.4%) (p<0.05).
Indoleacetic acid and siderophore production
Most of the isolates, altogether 91 strains, produced IAA (Table S1) ranging from 2.2 to 83.05 µg ml−1. Eleven strains produced more than 60 µg ml−1 IAA. Six of these were Ochrobactrum sp., three were Bacillus spp., one was Providencia sp. and one Rhizobium sp. Ochrobactrum sp. KT80 produced highest concentration (83.05 µg mL−1) of IAA among the 136 isolates, followed by Providencia sp. KT7 (79.02 µg mL−1) and Rhizobium sp. KT24 (75.82 µg ml−1).
Only 29 of the 136 isolates produced siderophore (Table S1) ranging from 5.50 to 167.67 µg ml−1. All the six Rhizobium sp. isolates that produced siderophore were IAA producers, whereas only half of the eighteen Bacillus spp. and two Ochrobactrum sp. siderophore producers produced IAA. Bacillus sp. isolates KT93 and KT113 that did not produce IAA produced highest siderophore concentrations of 167.67 µg ml−1 and 105.33 µg ml−1, respectively.
Basic physicochemical properties of the V-Ti magnetite mine tailing soil
The basic physicochemical properties are important factors for evaluating soil quality. The V-Ti magnetite tailing, a weakly acid soil, showed pH similar to that in an old Spanish Pb-Zn mine soil . Soil pH is the best predictor of microbial diversity and community composition , . The bacteria in the V-Ti magnetite mine tailing soil may prefer acid environment. The organic matter content of V-Ti magnetite mine tailing soil was lower than in agricultural and urban ecosystem soils , , but similar with other mine tailing area . The V-Ti magnetite mine tailing also showed lower content of available N, P and K than agricultural and urban ecosystem soils , , The low contents of available N, P, K and organic matter suggested that V-Ti magnetite mine tailing soil was unfertile. The iron, titanium and vanadium concentrations were up to three, ten and 70 times higher than in US soils in average , respectively. The concentrations of Cr, Zn, Cu, Ni and Mn were approximately 1.5 to 2.5 times higher than in US soils in average . The concentrations of Fe, Cu and Zn were above values considered very high by Abreu et al  and the chromium concentration was almost twice as high as needed to inhibit alfalfa germination , plausibly explaining the scarce vegetation at the Zhujiabaobao V-Ti magnetite tailing dam. Therefore, phytoremediation of the barren V-Ti magnetite mine tailing soil should include increasing the content of available N, P, K and organic matter and lowing metal concentration.
Genetic identification of bacterial isolates
To assess if the heavy metal-resistance and plant growth promoter-producing bacteria in the Zhujiabaobao V-Ti magnetite tailing dam soil would support phytoremediation, we isolated 136 bacterial strains, grouped them by BOX A1R-PCR and identified representative strains by 16S rRNA gene sequencing. The bacteria in the V-Ti magnetite mine tailing soil represented both Gram-negative and Gram-positive species. Bacillus spp. were the most abundant species, followed by Rhizobium spp. and Ochrobactrum spp. The spore and cyst forming capability of Bacillus spp. may explain why Bacillus spp. were abundant in the unfavorable environment of the V-Ti magnetite mine tailing soil. Autochthonous Bacillus from mine tailing in South Korea showed the ability to biomineralize heavy metals, such as Pb and Cr , . Ochrobactrum spp. and Pseudomonas spp. have been used for the bioremediation of environmental pollutants –. These observations suggested that the indigenous bacteria might be useful for phytoremediation of the Zhujiabaobao mine tailing soil. The presence of multiple autochthonous Rhizobium spp. implied that, with compatible leguminous plants, the rhizobium-legume symbiosis could be used to gradually increase nitrogen content and overall fertility in the barren soil. The symbiosis of rhizobia and leguminous plants has been effectively used to remediate contaminated soil , .
Heavy metal tolerance of bacterial isolates
To estimate the usefulness of the isolated bacteria in bioremediation, we assessed their heavy metal tolerance. Obviously, the bacteria in V-Ti magnetite mine soil have to tolerate the harsh environment polluted by heavy metals. The tolerance mechanisms include exclusion, extrusion, accommodation, bio-transformation and methylation or demethylation . Bacteria can enhance metal solubility by producing acid and detoxify metals by removal, sequestering or immobilizing . Since heavy metal tolerance is one of the most important factors for using an indigenous microorganism in bioremediation, recently the functional diversity of bacterial communities in contaminated soil has attracted more attention .
The bacterial isolates from V-Ti magnetite mine tailing soil showed diverse tolerance to different heavy metals. Most of the isolates did not tolerate the lowest tested concentration (200 mg kg−1) of Ni, Co and Zn. The concentrations of Ni and Zn were low in the mine tailing soil. A few of the V-Ti magnetite mine tailing isolates, e.g. Bacillus sp. KT87 and Bacillus sp. KT72, showed tolerance to higher metal concentrations than isolates from a copper mine tailing, from a mercuric salt-contaminated soil and from chickpea rhizosphere soil –. Interestingly, even though the concentration of Cd in the mine soil was not high, more than half the isolates tolerated a high concentration of Cd (1,000 mg kg−1). Likewise, even though the concentration of Pb in the mine tailing soil was low, some isolates tolerated a high concentration of Pb, i.e. the tolerance to heavy metals and the heavy metal content of soil did not directly correlate. Many mine tailing sites are polluted by multiple metals. For bacteria, the ability to survive, including variation in strains and characteristics, is related to environmental conditions and length of exposure to those conditions . Therefore, the isolates from the V-Ti magnetite mine tailing soil showing multi-metal resistance were affected by the unfavorable environment. The culturable bacteria included isolates with multiple heavy metal tolerance, especially among the Bacillus spp., suggesting that the indigenous bacteria are capable of assisting the bioremediation of the V-Ti magnetite mine tailing soil polluted by heavy metals.
Plant growth-promoting activity of bacteria
Plant-associated bacteria play a key role in host adaptation to changing environment by altering plant cell metabolism or promoting plant growth. Plant growth promoting rhizobacteria (PGPR) producing IAA and siderophore have been widely used to accelerate phytoremediation of metalliferous soil , . Production of indoleacetic acid (IAA), a phytohormone, is a key characteristic of PGPR . The addition of IAA to soil can enhance the uptake of metals in plant roots , , . Even though PGPR are widely studied, few studies have systematically analyzed PGPR in contaminated soil. About 23% and 50% of Zn- and Cd-accumulating isolates from a former zinc and lead mining and processing site in Austria produced IAA and siderophore, respectively . In V-Ti magnetite mine tailing soil the percentages of culturable rhizosphere IAA and siderophore producers were entirely different at 67% and 21%, respectively. The plant growth promoting activity of the isolates from the V-Ti magnetite mine tailing was stronger than that reported for Pseudomonas putida GR12-2 (IAA: 2.01 µg ml−1) from the rhizosphere of an arctic plant , but lower than that of Alcaligenes faecalis BCCM IC 2374 (Siderophore: 347 µg ml−1) , suggesting that the plant growth promoting activity from different environments is totally different. The abundance of isolates producing more than 20 µg ml−1 IAA suggested that the plant growth promoting ability of the isolates might assist in phytoremediating the soil.
The bacterial and fungal siderophores facilitate iron uptake in soil . Iron chelated by siderophores is unavailable to plant pathogens resulting in an increase in plant health . Metal–resistant siderophore-producing bacteria play important role in the successful survival and growth of plants in contaminated soil by alleviating metal toxicity and supplying nutrients for plant, and bacterial siderophore can bind metals other than iron , which may be the reason why microorganism can survive in the mine tailing soil contaminated by multi-metals. Bacterial siderophore should be beneficial to regulate availability of the abundant iron in the V-Ti magnetite mine tailing soil containing high concentration of iron. As bioaugmentation-assisted phytoextraction technology, the indigenous siderophore-producing bacteria can increase the phytoextraction rate that usually limits the use of phytoremediation methods . Aside from their involvement in iron acquisition, siderophores have physiological roles of protecting some bacteria against the toxic effect of pyochelin by reducing reactive oxygen species , so the presence of siderophore-producing bacteria in the mine tailing can directly or indirectly promote bioremediation for the contaminated soil. Many isolates showed both IAA and siderophore production, implying that the characteristics of the indigenous bacteria are helpful in bioremediating the desert mine tailing area. Phytoremediation of metals was facilitated by PGPR by promoting plant growth and increasing the amount of metal taken up by plant , .
The heavy metal-resistance and plant growth-promoting activity are key characteristics for bacteria that are to be applied in metal phytoremediation. Therefore, analyzing these characteristics in an indigenous bacterial in contaminated sites is essential to provide significant information for developing effective bioremediation measures. Moreover, because both the structural and functional bacterial diversity are important indicators of soil health, evaluation for diversity of heavy metal-resistant bacteria and PGPR should be considered as the primary work for bioremediating soil contaminated by heavy metals. We showed that V-Ti magnetite mine tailing soil in Zhujiabaobao contained abundant bacteria that tolerate multiple heavy metals and have plant growth-promoting abilities. The results suggested that the indigenous bacteria in the soil have characteristics beneficial for remediating the contaminated mine tailing soil. To further study the phytoremediation approach, the plant growth promoting activity will be studied both in greenhouses and in situ in Zhujiabaobao.
BOX-A1R dendrogram for 136 isolates from V-Ti magnetite mine tailing soil in Panzhihua, Sichuan, China.
Conceived and designed the experiments: XY QC. Performed the experiments: XY YL CZ HL JL WZ XK XL KZ QX. Analyzed the data: XY GY XZ QC. Contributed reagents/materials/analysis tools: XY QC. Contributed to the writing of the manuscript: XY.
- 1. Neuberger JS, Mulhall M, Pomatto MC, Sheverbush J, Hassanein RS (1990) Health problems in Galena, Kansas: a heavy metal mining Superfund site. Sci Total Environ 94: 261–272.
- 2. Saunders J, Jastrzembski B, Buckey J, Enriquez D, MacKenzie T, et al. (2012) Hearing loss and heavy metal toxicity in a Nicaraguan mining community: Audiological results and case reports. Audiol Neurootol 18: 101–113.
- 3. Ohlander J, Huber SM, Schomaker M, Heumann C, Schierl R, et al. (2013) Risk Factors for Mercury Exposure of Children in a Rural Mining Town in Northern Chile. PloS one 8: e79756.
- 4. Boularbah A, Schwartz C, Bitton G, Morel JL (2006) Heavy metal contamination from mining sites in South Morocco: 1. Use of a biotest to assess metal toxicity of tailings and soils. Chemosphere 63: 802–810.
- 5. Zhuang P, Lu H, Li Z, Zou B, McBride MB (2014) Multiple exposure and effects assessment of heavy metals in the population near mining area in South China. PloS one 9: e94484.
- 6. Mazej Z, Al Sayegh-Petkovšek S, Pokorny B (2010) Heavy metal concentrations in food chain of Lake Velenjsko jezero, Slovenia: an artificial lake from mining. Arch Environ Contam Toxicol 58: 998–1007.
- 7. Valverde A, González-Tirante M, Medina-Sierra M, Santa-Regina I, García-Sánchez A, et al. (2011) Diversity and community structure of culturable arsenic-resistant bacteria across a soil arsenic gradient at an abandoned tungsten–tin mining area. Chemosphere 85: 129–134.
- 8. Nielsen MN, Winding A (2002) Microorganisms as indicators of soil health. National Environmental Research Institute Denmark.
- 9. Gupta AK, Verma SK, Khan K, Verma RK (2013) Phytoremediation using aromatic plants: a sustainable approach for remediation of heavy metals polluted sites. Environ Sci Technol 47: 10115–10116.
- 10. Weyens N, van der Lelie D, Taghavi S, Newman L, Vangronsveld J (2009) Exploiting plant–microbe partnerships to improve biomass production and remediation. Trends Biotechnol 27: 591–598.
- 11. Fuentes-Ramirez LE, Jimenez-Salgado T, Abarca-Ocampo I, Caballero-Mellado J (1993) Acetobacter diazotrophicus, an indoleacetic acid producing bacterium isolated from sugarcane cultivars of Mexico. Plant Soil 154: 145–150.
- 12. Jaroszuk-Ściseł J, Kurek E, Trytek M (2014) Efficiency of indoleacetic acid, gibberellic acid and ethylene synthesized in vitro by Fusarium culmorum strains with different effects on cereal growth. Biologia 69: 281–292.
- 13. Khan MS, Zaidi A, Wani PA, Oves M (2009) Role of plant growth promoting rhizobacteria in the remediation of metal contaminated soils. Environ Chem Lett 7: 1–19.
- 14. Tak HI, Ahmad F, Babalola OO (2013) Advances in the application of plant growth-promoting rhizobacteria in phytoremediation of heavy metals. Reviews of Rev Environ Contam Toxicol 223: 33–52.
- 15. Leinhos V, Bergmann H (1995) Influence of auxin producing rhizobacteria on root morphology and nutrient accumulation of crops, pt. 2: root growth promotion and nutrient accumulation of maize (Zea mays L.) by inoculation with indole-3-acetic acid (IAA) producing pseudomonas strains and by exogenously applied IAA under different water supply conditions. Angewandte Botanik (Germany).
- 16. Lippmann B, Leinhos V, Bergmann H (1995) Influence of auxin producing rhizobacteria on root morphology and nutrient accumulation of crops, pt. 1: changes in root morphology and nutrient accumulation in maize (Zea mays L.) caused by inoculation with indole-3-acetic acid (IAA) producing Pseudomonas and Acinetobacter strains or IAA applied exogenously. Angewandte Botanik (Germany).
- 17. Rajkumar M, Freitas H (2008) Influence of metal resistant-plant growth-promoting bacteria on the growth of Ricinus communis in soil contaminated with heavy metals. Chemosphere 71: 834–842.
- 18. Olson JW, Mehta NS, Maier RJ (2001) Requirement of nickel metabolism proteins HypA and HypB for full activity of both hydrogenase and urease in Helicobacter pylori. Mol Microbiol 39: 176–182.
- 19. Sakamoto T, Bryant DA (2001) Requirement of nickel as an essential micronutrient for the utilization of urea in the marine cyanobacterium Synechococcus sp. PCC 7002. Plant Cell Physiol 42: 186.
- 20. Mishra VK, Upadhyaya AR, Pandey SK, Tripathi B (2008) Heavy metal pollution induced due to coal mining effluent on surrounding aquatic ecosystem and its management through naturally occurring aquatic macrophytes. Bioresour Technol 99: 930–936.
- 21. Ma Y, Prasad M, Rajkumar M, Freitas H (2011) Plant growth promoting rhizobacteria and endophytes accelerate phytoremediation of metalliferous soils. Biotechnol Adv 29: 248–258.
- 22. Zhou M-F, Robinson PT, Lesher CM, Keays RR, Zhang C-J, et al. (2005) Geochemistry, petrogenesis and metallogenesis of the Panzhihua gabbroic layered intrusion and associated Fe–Ti–V oxide deposits, Sichuan Province, SW China. J Petrol 46: 2253–2280.
- 23. Yanguo T, Shijun N, Xianguo T, Chengjiang Z, Yuxiao M (2002) Geochemical baseline and trace metal pollution of soil in Panzhihua mining area. Chinese J Geochemistry 21: 274–281.
- 24. Yanguo T, Xianguo T, Shijun N, Chengjiang Z, Zhengqi X (2003) Environmental geochemistry of heavy metal contaminants in soil and stream sediment in Panzhihua mining and smelting area, Southwestern China. Chinese J Geochemistry 22: 253–262.
- 25. Larsson MA, Baken S, Gustafsson JP, Hadialhejazi G, Smolders E (2013) Vanadium bioavailability and toxicity to soil microorganisms and plants. Environ Toxicol Chem 32: 2266–2273.
- 26. Kužel S, Hruby M, Cígler P, Tlustoš P, Van Nguyen P (2003) Mechanism of physiological effects of titanium leaf sprays on plants grown on soil. Biol Trace Elem Res 91: 179–189.
- 27. Eckardt NA (2012) Pumping iron: conserved iron deficiency responses in the plant lineage. Plant Cell 24(10): 3855.
- 28. Venail PA, Vives MJ (2013) Positive effects of bacterial diversity on ecosystem functioning driven by complementarity effects in a bioremediation context. PloS one 8: e72561.
- 29. Li Z, Zhang G, Liu Y, Wan K, Zhang R, et al. (2013) Soil nutrient assessment for urban ecosystems in Hubei, China. PloS one 8: e75856.
- 30. Zhang S, Chen M, Li T, Xu X, Deng L (2010) A newly found cadmium accumulator– Malva sinensis Cavan. J Hazard Mater 173: 705–709.
- 31. Chang S, Hsu H, Cheng J, Tseng C-P (2011) An efficient strategy for broad-range detection of low abundance bacteria without DNA decontamination of PCR reagents. PloS one 6: e20303.
- 32. Martin B, Humbert O, Camara M, Guenzi E, Walker J, et al. (1992) A highly conserved repeated DNA element located in the chromosome of Streptococcus pneumoniae. Nucleic Acids Res 20: 3479–3483.
- 33. Tacão M, Alves A, Saavedra MJ, Correia A (2005) BOX-PCR is an adequate tool for typing Aeromonas spp. Antonie van Leeuwenhoek 88: 173–179.
- 34. Miller CS, Handley KM, Wrighton KC, Frischkorn KR, Thomas BC, et al. (2013) Short-read assembly of full-length 16S amplicons reveals bacterial diversity in subsurface sediments. PloS one 8: e56018.
- 35. Wilson KH, Blitchington R, Greene R (1990) Amplification of bacterial 16S ribosomal DNA with polymerase chain reaction. J Clin Microbiol 28: 1942–1946.
- 36. Benson DA, Cavanaugh M, Clark K, Karsch-Mizrachi I, Lipman DJ, et al.. (2012) GenBank. Nucleic acids research: gks1195.
- 37. Tamura K, Stecher G, Peterson D, Filipski A, Kumar S (2013) MEGA6: molecular evolutionary genetics analysis version 6.0. Mol Biol Evol 30: 2725–2729.
- 38. Bric JM, Bostock RM, Silverstone SE (1991) Rapid in situ assay for indoleacetic acid production by bacteria immobilized on a nitrocellulose membrane. Appl Environ Microb 57: 535–538.
- 39. Patten CL, Glick BR (2002) Role of Pseudomonas putida indoleacetic acid in development of the host plant root system. Appl Environ Microb 68: 3795–3801.
- 40. Schwyn B, Neilands J (1987) Universal chemical assay for the detection and determination of siderophores. Analytical biochemistry 160: 47–56.
- 41. Murugappan R, Rekha S, Thirumurugan R (2006) Characterization and quantification of siderophores produced by Aeromonas hydrophila isolated from Cyprinus carpio. Pak J Biol Sci 9: 437–440.
- 42. Rodríguez L, Ruiz E, Alonso-Azcárate J, Rincón J (2009) Heavy metal distribution and chemical speciation in tailings and soils around a Pb–Zn mine in Spain. J Environ Manage 90: 1106–1116.
- 43. Tripathi BM, Kim M, Singh D, Lee-Cruz L, Lai-Hoe A, et al. (2012) Tropical soil bacterial communities in Malaysia: pH dominates in the equatorial tropics too. Microbial Ecol 64: 474–484.
- 44. Lauber CL, Hamady M, Knight R, Fierer N (2009) Pyrosequencing-based assessment of soil pH as a predictor of soil bacterial community structure at the continental scale. Appl Environ Microb 75: 5111–5120.
- 45. Brady NC, Weil RR (1996) The nature and properties of soils. Prentice-Hall Inc.
- 46. Shacklette HT, Boerngen JG (1984) Element concentrations in soils and other surficial materials of the conterminous United States.
- 47. Abreu CAd, van Raij B, Abreu MFd González AP (2005) Routine soil testing to monitor heavy metals boron. Sci Agr 62: 564–571.
- 48. Peralta-Videa J, Gardea-Torresdey J, Gomez E, Tiemann K, Parsons J, et al. (2002) Effect of mixed cadmium, copper, nickel and zinc at different pHs upon alfalfa growth and heavy metal uptake. Environ Pollut 119: 291–301.
- 49. Das S, Mishra J, Das SK, Pandey S, Rao DS, et al. (2014) Investigation on mechanism of Cr (VI) reduction and removal by Bacillus amyloliquefaciens, a novel chromate tolerant bacterium isolated from chromite mine soil. Chemosphere 96: 112–121.
- 50. Govarthanan M, Lee K-J, Cho M, Kim JS, Kamala-Kannan S, et al. (2013) Significance of autochthonous Bacillus sp. KK1 on biomineralization of lead in mine tailings. Chemosphere 90: 2267–2272.
- 51. Cheng Y, Yan F, Huang F, Chu W, Pan D, et al. (2010) Bioremediation of Cr (VI) and immobilization as Cr (III) by Ochrobactrum anthropi. Environ Sci Technol 44: 6357–6363.
- 52. Pandey S, Ghosh PK, Ghosh S, De TK, Maiti TK (2013) Role of heavy metal resistant Ochrobactrum sp. and Bacillus spp. strains in bioremediation of a rice cultivar and their PGPR like activities. J Microbiol 51: 11–17.
- 53. Wasi S, Tabrez S, Ahmad M (2013) Use of Pseudomonas spp. for the bioremediation of environmental pollutants: a review. Environ Monit Assess 185: 8147–8155.
- 54. Ike A, Sriprang R, Ono H, Murooka Y, Yamashita M (2007) Bioremediation of cadmium contaminated soil using symbiosis between leguminous plant and recombinant rhizobia with the MTL4 and the PCS genes. Chemosphere 66: 1670–1676.
- 55. Sriprang R, Hayashi M, Yamashita M, Ono H, Saeki K, et al. (2002) A novel bioremediation system for heavy metals using the symbiosis between leguminous plant and genetically engineered rhizobia. J Biotechnol 99: 279–293.
- 56. Pumpel T, Paknikar KM (2001) Bioremediation technologies for metal-containing wastewaters using metabolically active microorganisms. Adv Appl microbiol 48: 135–171.
- 57. Xie X, Fu J, Wang H, Liu J (2010) Heavy metal resistance by two bacteria strains isolated from a copper mine tailing in China. Afr J Biotechnol 9: 4056–4066.
- 58. Bafana A, Krishnamurthi K, Patil M, Chakrabarti T (2010) Heavy metal resistance in Arthrobacter ramosus strain G2 isolated from mercuric salt-contaminated soil. J Hazard Mater 177: 481–486.
- 59. Joseph B, Ranjan Patra R, Lawrence R (2012) Characterization of plant growth promoting rhizobacteria associated with chickpea (Cicer arietinum L.). Intl J Plant Prod 1: 141–152.
- 60. Roszak D, Colwell R (1987) Survival strategies of bacteria in the natural environment. Microbiol Rev 51: 365.
- 61. Ahmad F, Ahmad I, Khan M (2008) Screening of free-living rhizospheric bacteria for their multiple plant growth promoting activities. Microbiol Res 163: 173–181.
- 62. Leinhos V, Bergmann H (1995) Influence of auxin producing rhizobacteria on root morphology and nutrient accumulation of maize (Zea mays L.) by inoculation with indol-3-acetic acid (IAA) producing Pseudomonas strains and by exogenously applied IAA under different water supply conditions. Angew Bot 69: 37–42.
- 63. Kuffner M, De Maria S, Puschenreiter M, Fallmann K, Wieshammer G, et al. (2010) Culturable bacteria from Zn-and Cd-accumulating Salix caprea with differential effects on plant growth and heavy metal availability. J App Microbiol 108: 1471–1484.
- 64. Xie H, Pasternak J, Glick BR (1996) Isolation and characterization of mutants of the plant growth-promoting rhizobacterium Pseudomonas putida GR12–2 that overproduce indoleacetic acid. Curr Microbiol 32: 67–71.
- 65. Sayyed R, Chincholkar S (2010) Growth and siderophores production in Alcaligenes faecalis is regulated by metal ions. Indian H Microbiol 50: 179–182.
- 66. Rajkumar M, Ae N, Prasad MN, Freitas H (2010) Potential of siderophore-producing bacteria for improving heavy metal phytoextraction. Trends Biotechnol 28: 142–149.
- 67. Braud A, Jezequel K, Bazot S, Lebeau T (2009) Enhanced phytoextraction of an agricultural Cr- and Pb-contaminated soil by bioaugmentation with siderophore-producing bacteria. Chemosphere 74: 280–286.
- 68. Adler C, Corbalán NS, Seyedsayamdost MR, Pomares MF, de Cristóbal RE, et al. (2012) Catecholate siderophores protect bacteria from pyochelin toxicity. PloS one 7: e46754.
- 69. Glick BR (2010) Using soil bacteria to facilitate phytoremediation. Biotechnol Adv 28: 367–374.