Phytoremediation

Phytoremediation /ˌfaɪtəʊrɪˌmiːdɪˈeɪʃən/ (from Ancient Greek φυτό (phyto), meaning 'plant', and Latin remedium, meaning 'restoring balance') refers to the technologies that use living plants to clean up soil, air, and water contaminated with hazardous chemicals.[1]

Phytoremediation is a cost-effective plant-based approach of remediation that takes advantage of the ability of plants to concentrate elements and compounds from the environment and to metabolize various molecules in their tissues. It refers to the natural ability of certain plants called hyperaccumulators to bioaccumulate, degrade, or render harmless contaminants in soils, water, or air. Toxic heavy metals and organic pollutants are the major targets for phytoremediation. Knowledge of the physiological and molecular mechanisms of phytoremediation began to emerge in recent years together with biological and engineering strategies designed to optimize and improve phytoremediation. In addition, several field trials confirmed the feasibility of using plants for environmental cleanup.[2]

Application

Phytoremediation may be applied wherever the soil or static water environment has become polluted or is suffering ongoing chronic pollution. Examples where phytoremediation has been used successfully include the restoration of abandoned metal mine workings, and sites where polychlorinated biphenyls have been dumped during manufacture and mitigation of ongoing coal mine discharges reducing the impact of contaminants in soils, water, or air. Contaminants such as metals, pesticides, solvents, explosives,[3] and crude oil and its derivatives, have been mitigated in phytoremediation projects worldwide. Many plants such as mustard plants, alpine pennycress, hemp, and pigweed have proven to be successful at hyperaccumulating contaminants at toxic waste sites.

Over the past 20 years, this technology has become increasingly popular and has been employed at sites with soils contaminated with lead, uranium, and arsenic. While it has the advantage that environmental concerns may be treated in situ; one major disadvantage of phytoremediation is that it requires a long-term commitment, as the process is dependent on a plant's ability to grow and thrive in an environment that is not ideal for normal plant growth.

Advantages and limitations

Various processes

Phytoremediation process

A range of processes mediated by plants or algae are useful in treating environmental problems:

Phytoextraction

Phytoextraction (or phytoaccumulation) uses plants or algae to remove contaminants from soils, sediments or water into harvestable plant biomass (organisms that take larger-than-normal amounts of contaminants from the soil are called hyperaccumulators). Phytoextraction has been growing rapidly in popularity worldwide for the last twenty years or so. In general, this process has been tried more often for extracting heavy metals than for organics. At the time of disposal, contaminants are typically concentrated in the much smaller volume of the plant matter than in the initially contaminated soil or sediment. 'Mining with plants', or phytomining, is also being experimented with:

The plants absorb contaminants through the root system and store them in the root biomass and/or transport them up into the stems and/or leaves. A living plant may continue to absorb contaminants until it is harvested. After harvest, a lower level of the contaminant will remain in the soil, so the growth/harvest cycle must usually be repeated through several crops to achieve a significant cleanup. After the process, the cleaned soil can support other vegetation.

Advantages

The main advantage of phytoextraction is environmental friendliness. Traditional methods that are used for cleaning up heavy metal-contaminated soil disrupt soil structure and reduce soil productivity, whereas phytoextraction can clean up the soil without causing any kind of harm to soil quality. Another benefit of phytoextraction is that it is less expensive than any other clean-up process.

Disadvantages

As this process is controlled by plants, it takes more time than anthropogenic soil clean-up methods.

Two versions

Examples

Phytostabilization

Phytostabilization focuses on the long term stabilization and containment of the pollutant. For example, the plant's presence can reduce wind erosion; or the plant's roots can prevent water erosion, immobilize the pollutants by adsorption or accumulation, and provide a zone around the roots where the pollutant can precipitate and stabilize. Unlike phytoextraction, phytostabilization focuses mainly on sequestering pollutants in soil near the roots but not in plant tissues. Pollutants become less bioavailable, and livestock, wildlife, and human exposure is reduced. An example application of this sort is using a vegetative cap to stabilize and contain mine tailings.[11]

Phytotransformation

In the case of organic pollutants, such as pesticides, explosives, solvents, industrial chemicals, and other xenobiotic substances, certain plants, such as Cannas, render these substances non-toxic by their metabolism.[12] In other cases, microorganisms living in association with plant roots may metabolize these substances in soil or water. These complex and recalcitrant compounds cannot be broken down to basic molecules (water, carbon-dioxide, etc.) by plant molecules, and, hence, the term phytotransformation represents a change in chemical structure without complete breakdown of the compound. The term "Green Liver" is used to describe phytotransformation,[13] as plants behave analogously to the human liver when dealing with these xenobiotic compounds (foreign compound/pollutant).[14][15] After uptake of the xenobiotics, plant enzymes increase the polarity of the xenobiotics by adding functional groups such as hydroxyl groups (-OH).

This is known as Phase I metabolism, similar to the way that the human liver increases the polarity of drugs and foreign compounds (drug metabolism). Whereas in the human liver enzymes such as cytochrome P450s are responsible for the initial reactions, in plants enzymes such as peroxidases, phenoloxidases, esterases and nitroreductases carry out the same role.[12]

In the second stage of phytotransformation, known as Phase II metabolism, plant biomolecules such as glucose and amino acids are added to the polarized xenobiotic to further increase the polarity (known as conjugation). This is again similar to the processes occurring in the human liver where glucuronidation (addition of glucose molecules by the UGT class of enzymes, e.g. UGT1A1) and glutathione addition reactions occur on reactive centres of the xenobiotic.

Phase I and II reactions serve to increase the polarity and reduce the toxicity of the compounds, although many exceptions to the rule are seen. The increased polarity also allows for easy transport of the xenobiotic along aqueous channels.

In the final stage of phytotransformation (Phase III metabolism), a sequestration of the xenobiotic occurs within the plant. The xenobiotics polymerize in a lignin-like manner and develop a complex structure that is sequestered in the plant. This ensures that the xenobiotic is safely stored, and does not affect the functioning of the plant. However, preliminary studies have shown that these plants can be toxic to small animals (such as snails), and, hence, plants involved in phytotransformation may need to be maintained in a closed enclosure.

Hence, the plants reduce toxicity (with exceptions) and sequester the xenobiotics in phytotransformation. Trinitrotoluene phytotransformation has been extensively researched and a transformation pathway has been proposed.[16]

Role of genetics

Breeding programs and genetic engineering are powerful methods for enhancing natural phytoremediation capabilities, or for introducing new capabilities into plants. Genes for phytoremediation may originate from a micro-organism or may be transferred from one plant to another variety better adapted to the environmental conditions at the cleanup site. For example, genes encoding a nitroreductase from a bacterium were inserted into tobacco and showed faster removal of TNT and enhanced resistance to the toxic effects of TNT.[17] Researchers have also discovered a mechanism in plants that allows them to grow even when the pollution concentration in the soil is lethal for non-treated plants. Some natural, biodegradable compounds, such as exogenous polyamines, allow the plants to tolerate concentrations of pollutants 500 times higher than untreated plants, and to absorb more pollutants.

Hyperaccumulators and biotic interactions

A plant is said to be a hyperaccumulator if it can concentrate the pollutants in a minimum percentage which varies according to the pollutant involved (for example: more than 1000 mg/kg of dry weight for nickel, copper, cobalt, chromium or lead; or more than 10,000 mg/kg for zinc or manganese).[18] This capacity for accumulation is due to hypertolerance, or phytotolerance: the result of adaptative evolution from the plants to hostile environments through many generations. A number of interactions may be affected by metal hyperaccumulation, including protection, interferences with neighbour plants of different species, mutualism (including mycorrhizae, pollen and seed dispersal), commensalism, and biofilm.

Table of hyperaccumulators

Phytoscreening

As plants are able to translocate and accumulate particular types of contaminants, plants can be used as biosensors of subsurface contamination, thereby allowing investigators to quickly delineate contaminant plumes.[19][20] Chlorinated solvents, such as trichloroethylene, have been observed in tree trunks at concentrations related to groundwater concentrations.[21] To ease field implementation of phytoscreening, standard methods have been developed to extract a section of the tree trunk for later laboratory analysis, often by using an increment borer.[22] Phytoscreening may lead to more optimized site investigations and reduce contaminated site cleanup costs.

See also

References

  1. ↑ Reichenauer TG, Germida JJ (2008). "Phytoremediation of organic contaminants in soil and groundwater". Chemsuschem. 1 (8-9): 708–17. PMID 18698569. doi:10.1002/cssc.200800125.
  2. ↑ Salt DE, Smith RD, Raskin I (1998). "PHYTOREMEDIATION". Annual Review of Plant Physiology and Plant Molecular Biology. 49: 643–668. PMID 15012249. doi:10.1146/annurev.arplant.49.1.643.
  3. ↑ Phytoremediation of soils using Ralstonia eutropha, Pseudomas tolaasi, Burkholderia fungorum reported by Sofie Thijs
  4. ↑ Rupassara, S. I.; Larson, R. A.; Sims, G. K. & Marley, K. A. (2002), "Degradation of Atrazine by Hornwort in Aquatic Systems", Bioremediation Journal, 6 (3): 217–224, doi:10.1080/10889860290777576.
  5. ↑ Evans, Gareth M.; Furlong, Judith C. (2010-01-01). Phytotechnology and Photosynthesis. John Wiley & Sons, Ltd. pp. 145–174. ISBN 9780470975152. doi:10.1002/9780470975152.ch7/summary.
  6. ↑ Marchiol, L.; Fellet, G.; Perosa, D.; Zerbi, G. (2007), "Removal of trace metals by Sorghum bicolor and Helianthus annuus in a site polluted by industrial wastes: A field experience", Plant Physiology and Biochemistry, 45 (5): 379–87, PMID 17507235, doi:10.1016/j.plaphy.2007.03.018
  7. ↑ Wang, J.; Zhao, FJ; Meharg, AA; Raab, A; Feldmann, J; McGrath, SP (2002), "Mechanisms of Arsenic Hyperaccumulation in Pteris vittata. Uptake Kinetics, Interactions with Phosphate, and Arsenic Speciation", Plant Physiology, 130 (3): 1552–61, PMC 166674 Freely accessible, PMID 12428020, doi:10.1104/pp.008185
  8. ↑ Greger, M. & Landberg, T. (1999), "Using of Willow in Phytoextraction", International Journal of Phytoremediation, 1 (2): 115–123, doi:10.1080/15226519908500010.
  9. ↑ Adler, Tina (July 20, 1996). "Botanical cleanup crews: using plants to tackle polluted water and soil". Science News. Retrieved 2010-09-03.
  10. ↑ Meagher, RB (2000), "Phytoremediation of toxic elemental and organic pollutants", Current Opinion in Plant Biology, 3 (2): 153–162, PMID 10712958, doi:10.1016/S1369-5266(99)00054-0.
  11. ↑ Mendez MO, Maier RM (2008), "Phytostabilization of Mine Tailings in Arid and Semiarid Environments—An Emerging Remediation Technology", Environ Health Perspect, 116 (3): 278–83, PMC 2265025 Freely accessible, PMID 18335091, doi:10.1289/ehp.10608, archived from the original on 2008-10-24.
  12. 1 2 Kvesitadze, G.; et al. (2006), Biochemical Mechanisms of Detoxification in Higher Plants, Berlin, Heidelberg: Springer, ISBN 978-3-540-28996-8
  13. ↑ Sanderman, H. (1994), "Higher plant metabolism of xenobiotics: the "green liver" concept", Pharmacogenetics, 4: 225–241, doi:10.1097/00008571-199410000-00001.
  14. ↑ Burken, J.G. (2004), "2. Uptake and Metabolism of Organic Compounds: Green-Liver Model", in McCutcheon, S.C.; Schnoor, J.L., Phytoremediation: Transformation and Control of Contaminants, A Wiley-Interscience Series of Texts and Monographs, Hoboken, NJ: John Wiley, p. 59, ISBN 0-471-39435-1, doi:10.1002/047127304X.ch2
  15. ↑ Ramel, F., Sulmon, C., Serra, A.A., Gouesbet, G., Couée I. (2012), “Xenobiotic sensing and signalling in higher plants”, Journal of Experimental Botany, 63(11):3999-4014, doi: 10.1093/jxb/ers102, PMID 22493519
  16. ↑ Subramanian, Murali; Oliver, David J. & Shanks, Jacqueline V. (2006), "TNT Phytotransformation Pathway Characteristics in Arabidopsis: Role of Aromatic Hydroxylamines", Biotechnol. Prog., 22 (1): 208–216, PMID 16454512, doi:10.1021/bp050241g.
  17. ↑ Hannink, N.; Rosser, S. J.; French, C. E.; Basran, A.; Murray, J. A.; Nicklin, S.; Bruce, N. C. (2001), "Phytodetoxification of TNT by transgenic plants expressing a bacterial nitroreductase", Nature Biotechnology, 19 (12): 1168–72, PMID 11731787, doi:10.1038/nbt1201-1168.
  18. ↑ Baker, A. J. M.; Brooks, R. R. (1989), "Terrestrial higher plants which hyperaccumulate metallic elements – A review of their distribution, ecology and phytochemistry", Biorecovery, 1 (2): 81–126.
  19. ↑ Burken, J.; Vroblesky, D.; Balouet, J.C. (2011), "Phytoforensics, Dendrochemistry, and Phytoscreening: New Green Tools for Delineating Contaminants from Past and Present", Environmental Science & Technology, 45 (15): 6218–6226, doi:10.1021/es2005286.
  20. ↑ Sorek, A.; Atzmon, N.; Dahan, O.; Gerstl, Z.; Kushisin, L.; Laor, Y.; Mingelgrin, U.; Nasser, A.; Ronen, D.; Tsechansky, L.; Weisbrod, N.; Graber, E.R. (2008), ""Phytoscreening": The Use of Trees for Discovering Subsurface Contamination by VOCs", Environmental Science & Technology, 42 (2): 536–542, doi:10.1021/es072014b.
  21. ↑ Vroblesky, D.; Nietch, C.; Morris, J. (1998), "Chlorinated Ethenes from Groundwater in Tree Trunks", Environmental Science & Technology, 33 (3): 510–515, doi:10.1021/es980848b.
  22. ↑ Vroblesky, D. (2008). "User's Guide to the Collection and Analysis of Tree Cores to Assess the Distribution of Subsurface Volatile Organic Compounds".

Bibliography

This article is issued from Wikipedia. The text is licensed under Creative Commons - Attribution - Sharealike. Additional terms may apply for the media files.