Yue Wang1
Mathiyazhagan Narayanan
Zhenlun Li
Ying Ma- 1College of Resources and Environment, Southwest University, Chongqing, China
- 2Division of Research and Innovation, Department of Biotechnology, Saveetha School of Engineering, Saveetha Institute of Medical and Technical Science, Chennai, Tamil Nadu, India
- 3Department of Biotechnology, Periyar University, Salem, Tamil Nadu, India
Heavy metal contamination in soils endangers humans and the biosphere by reducing agricultural yield and negatively impacting ecosystem health. In recent decades, this issue has been addressed and partially remedied through the use of “green technology,” which employs metal-tolerant plants to clean up polluted soils. Furthermore, the global climate change enhances the negative effects of climatic stressors (particularly drought, salinity, and extreme temperatures), thus reducing the growth and metal accumulation capacity of remediating plants. Plant growth-promoting bacteria (PGPB) have been widely introduced into plants to improve agricultural productivity or the efficiency of phytoremediation of metal-contaminated soils via various mechanisms, including nitrogen fixation, phosphate solubilization, phytohormone production, and biological control. The use of metal-tolerant plants, as well as PGPB inoculants, should hasten the process of moving this technology from the laboratory to the field. Hence, it is critical to understand how PGPB ameliorate environmental stress and metal toxicity while also inducing plant tolerance, as well as the mechanisms involved in such actions. This review attempts to compile the scientific evidence on this topic, with a special emphasis on the mechanism of PGPB involved in the metal bioremediation process [plant growth promotion and metal detoxification/(im)mobilization/bioaccumulation/transformation/translocation] and deciphering combined stress (metal and climatic stresses) tolerance.
Introduction
Soil contaminated with heavy metals has become a serious worldwide problem due to geologic and anthropogenic activities, such as mining, fossil fuel combustion, application of agrochemicals, and so on. As heavy metals are non-biodegradable and extremely persistent in the environment, they can easily accumulate in different foods. Metal contamination of various foods, such as crops, meat, fish, milk, and eggs, threatens food safety. Metals contaminate agricultural soils, irrigation water, plants, and animals, resulting in their incorporation into the food chain and posing a significant threat to human health and ecosystems (Abdel-Rahman, 2022). The major sources of heavy metals and their harmful effects are summarized in Table 1. There are currently numerous methods for controlling heavy metal pollution. The advantages and disadvantages of different techniques are summarized in Table 2. Traditional remediation technologies for contaminated soil, such as cleaning, heat treatment, electrochemistry, and amendment application, often have complex processes that easily destroy soil structure and fertility. They are ineffective for treating both low concentration and large-scale heavy metal contamination in soils. Phytoremediation is a potential solution for remediating metal-polluted soils since it is a cost-effective plant-based approach (Ma et al., 2016a). During global climate change scenarios, plants are more severely and frequently subjected to episodes of climatic stress, such as high temperature, drought, and salinity, limiting their growth and performance. Furthermore, the direct (e.g., competition of ions) or indirect (e.g., alteration of soil physicochemical-biological properties) impact of climate change on metal bioavailability in soils may impede plant adaptation, making them more susceptible to stress and thus limiting the widespread application of phytoremediation (Rajkumar et al., 2013). Plant beneficial microorganisms (PBM), particularly plant growth-promoting bacteria (PGPB) create symbiotic relationships with plants, alleviating the toxicity of heavy metals, promoting multimodal tolerance of plants to metals and climatic stresses, and affecting the bioavailability of metals in soils (Ma et al., 2016b). For instance, PGPB can alleviate metal toxicity and alter metal bioavailability in soils through metal biosorption, bioaccumulation, redox reaction, mobilization, precipitation, and transformation (Ma et al., 2016a). They can also provide plants with multiplex tolerance to a variety of climatic stresses (such as drought and high salinity) by producing 1-aminocyclopropane-1-carboxylate deaminase (ACCD), siderophore, and phytohormone, and dissolving insoluble mineral nutrients (such as nitrogen, phosphorus, and potassium). These PGPB strains could also protect plants from phytopathogens by producing antibiotics and inducing induced systemic resistance (Grover et al., 2021). Understanding the interaction between plants and PBM has lots of potential for accelerating metal phytoremediation under various environmental stressors (e.g., salinity, drought, and extreme temperature). There have been very few investigations on plant-microbe associations for bioremediation of metal-polluted soils under climatic stresses.
Table 1. The sources and harmful effects of metals.
Table 2. Advantages and disadvantages of the available remediation techniques for metal-contaminated soils.
The current review has discussed the underlying mechanisms of PGPB involved in the heavy metal bioremediation in response to metal alone or in combination with climatic conditions (e.g., drought, salt, and heat) have been discussed. The main objective is to provide an overview of recent advances in developing PGPB-assisted phytoremediation under various climatic stresses, including the strategies to improve remediating plants tolerance and biomass, metal detoxification, bioaccumulation, transformation, and translocation activities. This review also emphasizes the commercial application of PGPB to improve phytoremediation efficiency.
Metal-resistant plant growth-promoting bacteria
Plant growth-promoting bacteria are a type of bacteria that may colonize rhizosphere soils and plant tissues and stimulate plant growth through various plant growth-promoting (PGP) activities under different conditions (Hashem et al., 2019). PGPB can improve plant abiotic and biotic stress tolerance by directly modulating phytohormone levels and facilitating resource acquisition, and/or indirectly by protecting plants against phytopathogens through the production of antibiotics and siderophores (Backer et al., 2018). They may act as free-living or rhizosphere bacteria (that form specific symbiotic relationships with roots), endophytic bacteria (that can colonize plant interior tissues), Rhizobia spp., and cyanobacteria (Glick et al., 2012). Figure 1 shows the type of plant growth-promoting bacteria. They all use the same PGP methods (direct and indirect); however, there are distinctions among these bacteria. Endophytic bacteria are more valuable in real-world applications than rhizobacteria because of their stable living environment and closer contact with plants for nutrient supply (Afzal et al., 2019). It has been reported that a group of metal-resistant PGPB, such as Pseudomonas, Arthrobacter, Agrobacterium, Bacillus, Azoarcus, Azospirillum, Azotobacter, Burkholderia, Klebsiella, Alcaligenes, Serratia, Rhizobium, and Enterobacter species have great potential to promote the growth of various plants in the metal-contaminated environments (Enebe and Babalola, 2018). These metal-resistant PGPB were found to enhance plant metal tolerance by improving detoxification rates of plants, enzymes secreted by plant roots, and soil pH modification (Guo et al., 2020). Moreover, certain metal-resistant PGPB can also alter metal mobility and bioavailability, and consequently plant usage rate by releasing chelating agents, acidification, and redox changes (Verma and Kuila, 2019). Therefore, these metal-resistant PGPB strains can be used as a suitable candidate for metal phytoremediation to minimize the adverse impact of metals and enhance metal accumulation capacity of plants. A number of metal-resistant PGPB have been reported to improve plant bioaccumulation/phytoextraction capacity through the secretion of siderophores and organic acids, which improve metal bioavailability by reducing soil pH (Manoj et al., 2020). In contrast, some metal-resistant PGPB can release polymeric substances (such as glomalin and polysaccharides) that speed up metal phytostabilization by limiting their mobility (Ma et al., 2016a).
Figure 1. Type of plant growth-promoting bacteria (Glick et al., 2012).
However, microbes have a strong dependence on the environment, and changes in environmental conditions can modulate the diversity, abundance, and functioning of bacteria (Afzal et al., 2019). Sánchez-Marañón et al. (2017) studied bacterial communities in eight soils selected along a soil-forming gradient and found that distinct bacterial distributions were positively connected to organic carbon, water-stable aggregates, porosity, water, and acidity. Furthermore, endophytic microbiota can be influenced by the age, genotype, nutritional status, and geographical location of the host plants (Ahmed et al., 2020). Carvalhais et al. (2013) confirmed that the transcriptional changes of B. amyloliquefaciens caused by the nutrient-deficient corn exudates were significantly correlated with the concentrations of amino acids, aspartic acid, valine, and glutamic acid in the root exudates. Furthermore, differences in microbial communities can result from host plant preferences for stress conditions. Wu et al. (2020a) reported the growth of B. subtilis at high salinity reduces the cell expansion pressure due to the passage of water through an osmotic gradient. Similarly, Xu et al. (2018) also demonstrated that drought delayed the development of early root microbiota in Sorghum bicolor. Nevertheless, inoculation of climatic stress-resistant PGPB has great potential to increase plant resistance/tolerance to such environmental stresses. Bruno et al. (2020) pointed out that Bacillus cereus improved the growth of S. bicolor and its phytoremediation potential in Cr-contaminated soil at elevated atmospheric temperature by producing siderophores and indole-3-acetic acid (IAA).
Mechanisms of PGPB in remediation of metal-contaminated soils under various climatic stresses
The microbiome is essential for plant growth and function, particularly PGPB play a key role in plant growth regulation via phytohormone production, plant nutrient acquisition, and abiotic and biotic stress alleviation, which enable plants to tolerate high concentrations of heavy metals and thus better survive in challenging conditions. Figure 2 depicts the mechanism of the synergistic effect of PGPB on the phytoremediation of metal-contaminated soils. PGPB could promote plant growth directly and/or indirectly under metal stress. The direct plant growth promotion by PGPB involves producing phytohormones (e.g., auxin, cytokinin, gibberellin, abscisic acid, and ethylene), or facilitating plant nutrient uptake (e.g., nitrogen, phosphorus, potassium, etc.; Figure 2A). Since the interaction between the antibacterial activity of PGPB and nutrient competition inhibits the growth of pathogenic bacteria, the production of antibacterial compounds and the coexistence of pathogens enhance ISR and indirectly promote plant growth (Figure 2B). One or more of these mechanisms can be used by specific PGPB to enhance plant resistance to environmental stresses. PGPB also can adsorb metals through coordinate, chelate, and ion exchange. Under climatic stresses, PGPB can also effectively change metal bioavailability through mobilization, stabilization, and transformation, thereby improving bioremediation efficiency and reducing the climatic stress effect by regulating the antioxidant enzyme activity and ion balance in plants (Figure 2C).
Figure 2. Mechanism of the synergistic effects of PGPB on the bioremediation of metal-contaminated soils. (A) Direct mechanism of plant growth promotion; (B) Indirect mechanism of plant growth promotion; (C) Mechanism of PGPB affecting metal under abiotic stress.
Resistance mechanism of PGPB in alleviating stress in plants
The biomass of remediating plants and soil metal bioavailability are key factors influencing phytoremediation efficiency. Nitrogen, phosphorus, potassium, and other minerals are essential nutrients for plant growth. Although there are many phosphorus and potassium elements present in soils, most of them are insoluble and not bioavailable for plants. The existence of metals can aggravate the loss of nutrients in soils, making them unable to be effectively absorbed and utilized by plants (Ashraf et al., 2017; Ahemad, 2019). Metals can also have a significant impact on plant growth and development. Many studies have shown that when plants are grown under metal stress conditions, the membrane system of plants is damaged, and then the structure and function of organelles are affected, and various physiological and biochemical processes (such as chlorophyll content, photosynthesis rate, biomass reduction, and so on) in their tissues are impaired (Zhu et al., 2020). In metal-contaminated soil, PGPB can improve plant tolerance to such stresses (metal and other climatic stresses) and stimulate plant growth by maintaining nutrient status and adjusting phytohormonal balance through the production of plant growth regulators. Several studies have indicated that PGPB contributes significantly to phytohormone production, which can not only regulate plant growth, regular development, and physiological processes and but also control biological and non-biological stress responses (Afzal et al., 2019; Hewage et al., 2020). Chen et al. (2017) reported that under the stress of Zn and Cd, Pseudomonas fluorescens can promote the growth and physiological indicators (above ground chlorophyll and enzyme activity) of Sedum alfredii by producing IAA, and improve plant Cd absorption by regulating the expression and transport genes of Cd. Furthermore, some IAA-producing PGPB could increase plant uptake of nutrients and water and reduce the stress effects of salt and drought on plants by changing the roots system architecture (Etesami and Maheshwari, 2018). Pan et al. (2019) demonstrated the potential of abscisic acid (ABA)-producing B. subtilis to minimize Cd accumulation in Arabidopsis thaliana. A number of bacteria with gibberellin acid production capacity alleviate metal toxicity by reducing Cd uptake and lipid peroxidation, altering hormonal balance, and regulating activities of proteases, catalase, and peroxidase (Etesami, 2018). Moreover, PGPB containing ACCD can help plants to cleave the synthesis ethylene precursor 1-aminocyclopropane-1-carboxylate by metabolizing it into α-butanone acid and ammonia, thereby alleviating the ethylene level in plants and improving their climatic stress tolerance (Vejan et al., 2016).
Microorganisms can also improve plant growth directly via nitrogen fixation, phosphorus dissolution, and potassium dissolution (Ashraf et al., 2017). Stenotrophomonas rhizophila and B. amyloliquefaciens were able to fix nitrogen, thus providing abundant nitrogen to Brassica napus (Liu et al., 2021). Besides, certain PGPB like Klebsiella variicola can convert insoluble phosphate to soluble forms through the secretion of enzymes (phosphonates and C–P lyases) and organic acids (citric acid oxalic, fumaric, and malic; Manoj et al., 2020), thereby improving the phosphorus availability in the rhizosphere under metal stress. Potassium-solubilizing bacteria can form biofilms on the surface of rhizosphere minerals by producing capsular polysaccharides, hydroxyl anions, iron carriers, and extracellular enzymes, as well as dissolve K-containing minerals in soils and effectively release K by synthesizing organic and inorganic acids (Etesami and Maheshwari, 2018). Many recent investigations have revealed that a number of PGPB, namely Pseudomonas, Bacillus, Klebsiella, and Pantoea, can release K from insoluble minerals such as mica and illite through a variety of mechanisms (including acidolysis, chelation, exchange reactions, and complexolysis), including the production of organic acids (Bakhshandeh et al., 2017). Some microorganisms can absorb iron from the siderophore-Fe complex through chelation degradation and release of iron, direct uptake of siderophore-Fe complex and ligand exchange (Ma et al., 2016b). Agarwal et al. (2020) found that Staphylococcus warneri GL1, B. velezensis GL3, GL5, and GMC2, isolated from Gnetum gnemon, are able to secrete various siderophores with high affinity for Fe3+, effectively inhibiting the growth of Ralstonia solanacearum in the rhizosphere.
Over the past 2 decades, there has been a better understanding of antibiotics as the basis of the biological control mechanism of PGPB and a variety of antibiotics have been identified such as amphibious steroids, 2,4-diacetylphloroglucinol, hydrogen cyanide (HCN), oomycin A, phenazine, pyoluteorin, pyrrolidin tensin, and troponin (Compant et al., 2005). Pseudomonas fluorescens can inhibit the root rot of Nicotiana tabacum caused by Thielaviopsis basicola by synthesizing pyocyanin and 2,4-diacetyl fluorescein (Morales-Cedeño et al., 2021). Competition is one of the important mechanisms of PGPB’s resistance, including nutrition competition and locus competition. Through high-density colonization in plant rhizosphere or tissues, PGPB competes with indigenous microorganisms in the same micro-environment for oxygen, nutrition, and space (Compant et al., 2005). Induced systemic resistance (ISR) is the term being used for microbe-mediated induce plant resistance to infection by pathogenic fungi, bacteria, viruses, nematodes, and pests (Manoj et al., 2020). ISR is a central mechanism for Pseudomonas, Trichoderma, and Bacillus to protect plant against various pathogens (Saeed et al., 2021). In addition, lipopolysaccharide, flagellum and siderophores produced by PGPB can also cause ISR in plants (Ahmed et al., 2020). Inoculation with hydrogen cyanide-producing Brevibacterium casei MH8a significantly increased the biomass and accumulation of Cd, Zn, and Cu in Sinapis alba (Plociniczak et al., 2016). This is probably due to the potential of bacterial HCN to enhance plant growth and metal mobilization (Manoj et al., 2020). Recently, the release of stress-related volatile compounds was also found to increase plant biomass, yield, and survival under water stress (Etesami and Glick, 2020).
Mechanism of action of PGPB on heavy metals
Climatic stresses have a significant impact on metal bioavailability. For instance, extreme temperatures can disrupt the nutrient and metal pathway by dissolving organic matter, decomposing microbial cells and destroying soil aggregates, and altering metal bioavailability, absorption, and distribution in plant tissues (Rajkumar et al., 2013). Li et al. (2011) found that higher temperature increased Cd accumulation in roots while decreased root elongation of Triticum aestivum in Cd-contaminated soils. This is because higher temperatures increased Cd toxicity to plant roots by increasing Cd accumulation and changing the subcellular distribution of Cd. Furthermore, changes in soil moisture can affect soil pH, EH, calcium carbonate, soluble organic content, and the electrochemical characteristics of the soil surface, all of which have an indirect impact on metal distribution in the soil solid–liquid phase and thus metal bioavailability. Pascual et al. (2004) noticed lower bioavailability of Zn, Cu, Mn, and Ni concentrations in soils when water was scarce. This was ascribed to a lower rate of soil mineralization as a result of drought stress. In response, increased metal deposition in the leaves has the ability to improve drought stress resistance and delay the negative consequences by reducing stratum corneum transpiration or increasing osmotic pressure in cells (Rajkumar et al., 2013).
Metal mobilization
Heavy metals are commonly present in both bioavailable and non-bioavailable forms in soils. The mobility and solubility of metals in soils are considered to be important factors influencing plant extraction efficiency (Ma et al., 2016b). Metal-resistant PGPB can mobilize metals and thus increase metal availability in the soil environment by secreting various organic acids (such as oxalic acid, acetic acid, and citric acid) and biosurfactants. Wu et al. (2018) noted that the inoculation of Buttiauxella sp. SaSR13 increased the content of root exudates (especially malic and oxalic acids) of S. alfredii, resulting in significant increases in the bioavailability and plant uptake of Cd. Additionally, biosurfactants can promote the entry of hydrophobic contaminants into the aqueous phase by solubilizing and micellizing the contaminants. These micelles and dissolved contaminants allow metal removal via soil washing or make them easily absorbed by plants (Akbari et al., 2018). Therefore, biosurfactant-producing microorganisms present in contaminated soils can effectively enhance metal mobility (Lal et al., 2018). San Martín et al. (2021) demonstrated that rhamnolipid-producing Pseudomonas Y3-B1A achieved a maximum vanadium removal efficiency of 85.5%.
Metal-resistant PGPB can also mobilize metal through biomethylation, leading to their volatilization. Certain PGPB can transfer methyl groups to metals (Pb and Se, etc.) to form methylated metal compounds with altered volatility, solubility, and toxicity (Ahemad, 2019). Microbial methylation of arsenic (As) raises trace levels of As species like monomethylarsinic acid and dimethylarsinic acid (DMA) in soils. Methylated As is absorbed by plant roots more slowly than inorganic As. DMA does not form compounds with plant chelating agents and is not quenched in vacuoles, allowing for efficient DMA transport inside the plants (Bali and Sidhu, 2021). Zhang et al. (2015) also proposed that As trioxide S-adenosylmethionine methyltransferase of Pseudomonas alcaligenes play a major role in the methylation and detoxification of As (III), which can be used in the bioremediation of As-contaminated environment.
Metal stabilization
The combination of metals with extracellular substances (e.g., anionic functional groups and extracellular polymers) can reduce metal bioavailability in soils, therefore reducing metal absorption or migration to aboveground plant parts. For instance, many metals can be efficiently immobilized in soils by combining with anionic functional groups on the cell surface (e.g., mercapto, carboxyl, hydroxyl, sulfonate, amine, and amide groups; Jacob et al., 2018). These substances reduce metal toxicity by forming complexes or effective barriers around cells (Ahemad, 2019). Some PGPB can also reduce metal bioavailability in soils through precipitation, alkalization, and complexation processes. The inorganic acids secreted by PGPB (e.g., hydrogen sulfide, bicarbonate, and phosphate) can also react rapidly with certain dissolved metals (Cu, Fe, Zn, and Pb) to form insoluble precipitates (Ma et al., 2016b).
Extracellular polymer substances (EPS) produced by PGPB are biosynthetic polymers composed mainly of polysaccharides, proteins, uronic acid, hummus, lipids, and other compounds. A previous study noted that bacterial EPS play a variety of biological activities in microbes and plants (Manoj et al., 2020). EPS generated by PGPB was shown to bind firmly to potentially harmful trace elements and capture precipitated metal sulfides and oxides to form organic metal complexes, enhancing resistance to toxic trace elements (Etesami and Maheshwari, 2018). The role of PGPB in the biosorption of Cs+ was confirmed by the production of EPS and biofilm formation of Nocardiopsis sp. (Sivaperumal et al., 2018). Silambarasan et al. (2019b) discovered that Rhodotorula sp. CAH2 could survive up to 6 mmol L−1 Al and produce EPS consisting of glucose, mannose, and galactose even under multiple stress conditions (salt and drought), along with the yield increasing as the stress level increased.
Phosphate solubilized by PGPB can also precipitate metals as metal accumulation in bacterial biomass is mediated by phosphatases that release inorganic phosphates from supplied organophosphate donor molecules (e.g., glycerol 2-phosphate) and metal cations precipitate on the biomass as phosphates (Gadd, 2004). In addition, microbial-induced carbonate precipitation (MICP) has been proposed as a viable bioremediation approach for metal immobilization. In MICP, carbonates can bind to the metals (e.g., Pb2+ and Cu2+) on the surface, after which these metal elements change from soluble forms to insoluble forms, thus reducing their toxicity (Tamayo-Figueroa et al., 2019). The MICP caused by B. pasteurii ATCC 11859 maintained the microbial growth while reducing the available Pb content in the soil, resulting in a decrease in Pb extraction and available Pb content by 76.34 and 41.65%, respectively (Chen et al., 2021).
Metal transformation
The valence state of the metal determines its toxicity. The oxidation–reduction process of metal by bacteria results in various chemical transformations of metal, affecting their shape and mobility in soils, which is regarded as an essential detoxifying mechanism (Ma et al., 2016b). Metal ions’ redox reactions can be regulated by PGPB via cell metabolism, and metals could be converted into non-bioavailable states in the rhizosphere to reduce their toxic effects on plants (Sharma, 2021). It has been found that variation in metal-reducing bacteria can catalyze the reduction reaction and use metal to replace Fe3+ and S0 as terminal electron receptors in anaerobic respiration (Yin et al., 2019).
Enzyme-mediated reduction in toxic metals to less destructive forms is another popular strategy for reducing metal toxicity, which helps to improve microbial resistance to metal ions. These enzymes cleave bonds and use the energy generated by biochemical reactions to assist in the transfer of electrons from one compound to another (Voica et al., 2016). Harmful pollutants are eventually oxidized to innocuous molecules as a result of these processes. Furthermore, these enzymes aid in the humification of various phenolic compounds produced by lignin degradation in the soil environment, as well as the detoxification of various xenobiotics, such as aniline or phenolic compounds via chemical interactions (Jacob et al., 2018). Giovanella et al. (2016) found that Pseudomonas B50A removed 86% of Hg in the medium. This is probably due to the fact that Hg (II) reductase produced by strain B50A could effectively reduce Hg (II) to Hg (0) to reduce its toxicity.
Metal detoxification
The metal detoxification processes induced by PGPB have a significant influence on phytoremediation efficiency. Metal biosorption and bioaccumulation by bacteria, as well as the synthesis of plant hormones, ACCD, and other secretions, have all been proven to improve plant resistance to metals (Etesami and Maheshwari, 2018; Yaashikaa et al., 2021). Biosorption and bioaccumulation of inorganic and organic pollutants are determined by interaction traits of biomass and concentration of pollutants. In biosorption, the contaminants adhere to the surface of the cell wall, whereas in bioaccumulation, the contaminants accumulate within the cells (Ma et al., 2016b; Priyadarshanee and Das, 2021). Huang et al. (2020a) found that B. subtilis had significant biosorption potential, since it adsorbed about 10–20 mg L−1 concentration of Cd2+. This type of biosorption phenomenon can reduce the pollutants (especially metals) toxicity to plants. In another study, Sedlakova-Kadukova et al. (2019) proved that Streptomyces K11 isolated from alkaline brown mud disposal site considerably reduced the Zn toxicity through extracellular accumulation and chelation, which are related to its Zn tolerance and high bioaccumulation efficiency.
Genetically modified organisms for bioremediation
The use of genetically engineered microorganisms (GEMs) is also a promising strategy to clean up metal-polluted soils. Transgenic methods are not only used to convert functional genes but also to elevate particularly recognized promoters to existing gene functions connected with metal accumulation/translocation/detoxification mechanisms and introduce them to target bacteria (Pratush et al., 2018). As a low molecular weight, cysteine-rich protein, metallothioneins (MTs) found in many bacteria have the ability to bind metals and form complex biochemical structures (Venegas-Rioseco et al., 2022). Some gene transformation experiments have convincingly demonstrated that MTS produced by PGPB (e.g., P. putida and Mycobacterium tuberculosis) can improve plant tolerance to metals (Mierek-Adamska et al., 2017; Nanda et al., 2019). Li et al. (2021) proved that E. coli cells expressing SUMO-ShMT3 bioaccumulated Cd2+, Cu2+, and Zn2+. The biofilm-forming marine bacterium P. aeruginosa N6P6 possessing the bmtA gene resisted a variety of metals (e.g., Pb, Cd, Hg, Cr, and Zn; Kumari and Das, 2019).
Since several elements in the promoter region of the metals responsive gene can be activated by plant hormones and growth regulators, the relationship between these regulator compounds and metal chelator phytochelatins is very important, which are in the first line of heavy metal defense mechanism is critical (Pal et al., 2018). Phytochelatins are enzymatically synthesized from glutathione by phytochelatin synthase activity in the presence of metal and their synthesis also initiates/transforms the entities of metal anions (Ag, Au, Cd, Cu, Hg, Pb, and Zn) and cations (As; Ozyigit et al., 2020). de Souza and Vicente (2020) proved that recombinant E. coli clones expressing the synthetic phytochelatin EC20 have higher Cd2+ biosorption capacity and tolerance than that without EC20. Heavy-metal ATPases (HMA), a subfamily of P-type HMA transporters, are found in a wide range of microorganisms. The energy released by ATP hydrolysis is mostly used to power the transmembrane transport of some metal ions, such as Ag+, Zn2+, Cd2+, Cu2+, and Ni2+ (Yang et al., 2022). Begum et al. (2019) showed that HSP70 and HMA3 genes (a member of the HMA family) were highly expressed in Panicum virgatum inoculated with P grimontii and P. vagans under Cd stress, resulting in an increase in the biomass and IAA yield in inoculated plants, but a decrease in Cd accumulation. Both the natural resistance-associated macrophage protein family and the yellow streak-like transporters are also responsible for the absorption, transport, and detoxification of transition metals (Chowdhury et al., 2021; Yang et al., 2022).
The application of these GEMs is a very effective method to remove pollutants from the environment. However, the application of GEMs can affect the natural ecosystem, posing risks to the environment (Hussain et al., 2018). GEMs are considered a competitive alien species to the ecosystem and their introduction may reduce microbial biodiversity in the ecosystem. Besides, they may have adverse effects on human health, causing cancer and other genetic diseases (Saravanan et al., 2022). Undoubtedly, GEMs have potential ecological risks, but it is possible to find an efficient way to implement GEMs in the bioremediation of metal-polluted soils in the future through technical safeguards and innovation. For instance, some countries have issued necessary guidelines for assessing and monitoring the risks of GEMs in the environment, emphasizing risk stratification when applying GEMs for bioremediation (Wu et al., 2021). There have been recent attempts to design and track GEMs including the development of a set of criteria for the utilization of GEMs (Ezezika and Singer, 2010). In addition, another containment approach mainly involves designing “suicidal GEMs,” when the pollutants are degraded, the killer gene is activated and the GEMs are then eradicated (Rebello et al., 2021).
Application and commercialization of PGPB in phytoremediation under environmental stress
The use of PGPB in bioremediation has become more and more popular due to their abilities to detoxify and degrade toxins and promote plant growth. Silambarasan et al. (2020) demonstrated that the inoculation with Pseudomonas citronellolis SLP6 improved bud and root growth (length, fresh, and dried biomass), chlorophyll content, antioxidant enzyme activity, and Cu uptake in roots and shoots under Cu and Cu+ salt stress. Interestingly, they concluded that the P. citronellolis SLP6 amalgamation could be an effective approach for phytostabilization in Cu-contaminated saline soils. Accordingly, Bruno et al. (2021) reported that the inoculation of multi-metal (MM) and increased atmospheric temperature (IAT) tolerant B. cereus TCU11 significantly improved the growth and phytoextraction (Pb, Zn, Ni, Cu, and Cd) potential of Zea mays in metal-contaminated soils. However, most PGPB applications in metal bioremediation are done in pot or greenhouse experiments, with in situ investigations in field conditions being rare. The field experiment conducted by Ren et al. (2019) showed that B. cepacia J62 increased the contents of ascorbic acid and glutathione in B. napus and reduced the oxidative stress caused by metals. The successful colonization contributed to increasing the biomass and the total Cu absorption (67.91%). Prapagdee and Khonsue (2015) found that the Cd accumulation in the root, ground tissue, and whole plant increased by 1.2-, 1.4-, and 1.1-fold, respectively, after inoculation of Arthrobacter sp. with Ocimum gratissimum for 2 months in the field conditions. The applications of PGPB in metal phytoremediation in the past 5 years are summarized in Table 3.
Table 3. Application of PGPB in bioremediation under environmental stress.
Furthermore, the use of microbial agents in soil bioremediation via bioaugmentation techniques would be extremely beneficial to the industrialization of microbial inoculum. Surprisingly, it also boosted the commercialization and market demand for various microbial inoculations. Microbial agents are abundant in high-activity beneficial PGPB, such as N-fixing bacteria and K-dissolving bacteria. These microorganisms’ metabolic activities can effectively reduce metal concentrations and toxicity in the environment (Ma et al., 2016a). Notably, B. subtilis has been produced and sold under the trade names RhizoVital® and FZB24® TB for use in alleviating environmental stress and promoting plant growth (Ngalimat et al., 2021). Pseudomonas fluorescens has also been used to produce commercial inoculants under the trade names Conquer and Victus (Suyal et al., 2016). Moreover, some inoculant products currently on the market contain several different microorganisms (O’Callaghan et al., 2020). Wang et al. (2020) noted that the combination of Enterobacter sp. and Comamonas sp. can efficiently fix Cd. In addition, various inorganic materials (mainly clay and talc), organic materials (peat, charcoal, and plant waste materials), and polymers (polysaccharides, protein, and synthetic polymers) were used as carriers for PGPB encapsulation (Szopa et al., 2022). Alginate hydrogels seem to be a successful commercial product. Su et al. (2021) noted that the maximum adsorption capacity of Cu on multilayer calcium alginate beads containing diatom bacteria and B. Subtilis can reach 141.34 mg g−1. Bacillus strains immobilized in alginate macrobeads were also found to enhance drought stress adaptation of Guinea grass (Mendoza-Labrador et al., 2021). Tu et al. (2020) used corn stalk biochar and Pseudomonas sp. as materials and illustrated the stabilization mechanism of biochar-loaded microbial inoculum on Cd-and Cu-contaminated soils.
Conclusion and future prospects
This review has addressed the mechanism of PGPB promoting plant growth and enhancing plant resistance under biotic and abiotic stress and the function in response to metal bioavailability and toxicity. This has significant scientific and practical implications for the use of PGPB in the phytoremediation of metal-contaminated soils as well as an understanding of the interaction between external pressure factors and biological processes. However, due to the nature of PGPB themselves, there are limitations in their utilization process. First, the genetic stability of PGPB is poor and easy to change, making them difficult to remove all pollutants. Second, there is a competitive survival relationship between PGPB and indigenous microbes, and eventually, these PGPB strains may be eliminated due to competitive failure. Finally, PGPB are easily affected by other factors such as external environment temperature, soil pH, and so on, thereby hampering the bioremediation efficiency. More research is needed to better understand the interaction between major factors namely metal, soil, microorganisms and plants.
We should pay close attention to how PGPB is employed in actual soil rehabilitation. Soil pH, humidity, and other environmental parameters could affect the efficiency of bioremediation. Compare with the studies of PGPB strain under laboratory conditions, the research on the field and in situ remediation experiments of PGPB strain under different environmental conditions is still very scarce.
The effects of different inoculation or application methods of PGPB on the phytoremediation efficiency of metal-polluted soil were explored. The appropriate inoculation method not only can change the soil nutritional status and directly affect PGPB survival and colonization efficiency but also can indirectly affect metal bioavailability in soils by changing the quantity and composition of root exudates of host plants.
There is a need to strengthen the utilization and safe disposal of post-remediation materials. Some bioaccumulating plants could produce certain harmful biomass after soil remediation. If these dry materials cannot be effectively treated, the original significance of bioremediation will be compromised. Therefore, the follow-up treatment of bioremediation technology and the recovery and treatment of metal in soils also have great research value.
It is necessary to develop additional research to analyze and anticipate how metals may influence plant development, metal accumulation, and ecophysiological responses in soils as a result of global climate change. The exact repercussions of climate change on plant–metal interactions in the future are difficult to anticipate due to the complicated interactions between various metals. Furthermore, much of the research lacks information on the behavioral dynamics and metabolomics of PGPB under environmental stresses. As a result, we need to improve our understanding of rhizosphere micro-ecological processes at the molecular level and choose the best couple of plants and PGPB to provide theoretical direction for long-term pollution decontamination.
Author contributions
YM developed the ideas and wrote the manuscript, and was the project sponsor. YW wrote the first draft of the manuscript. YM, MN, XS, XC, ZL, and DN revised the manuscript. All authors contributed to the article and approved the submitted version.
Funding
This work is carried out at the College of Resources and Environment, Southwest University, supported by the Fundamental Research Funds for the Central Universities (No. SWU 020010), the Natural Science Foundation of Chongqing (No. cstc2021jcyj-msxmX0827), and Chongqing Returned Overseas Students’ Entrepreneurship and Innovation Support Program (No. cx2021001).
Conflict of interest
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
Publisher’s note
All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.
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Keywords: plant growth-promoting bacteria, metal bioavailability, metal detoxification, climatic stresses, bioremediation
Citation: Wang Y, Narayanan M, Shi X, Chen X, Li Z, Natarajan D and Ma Y (2022) Plant growth-promoting bacteria in metal-contaminated soil: Current perspectives on remediation mechanisms. Front. Microbiol. 13:966226. doi: 10.3389/fmicb.2022.966226
Edited by:
Deniz Yildirim, Çukurova University, TurkeyReviewed by:
Dilek Alagöz, Çukurova University, TurkeyBaris Binay, Gebze Technical University, Turkey
Copyright © 2022 Wang, Narayanan, Shi, Chen, Li, Natarajan and Ma. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) and the copyright owner(s) are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: Ying Ma, Y2F0aHltYXlpbmdAaG90bWFpbC5jb20=