Open access peer-reviewed chapter

Phytoremediation: Halophytes as Promising Heavy Metal Hyperaccumulators

Written By

Kamal Usman, Mohammad A. Al-Ghouti and Mohammed H. Abu- Dieyeh

Submitted: November 18th, 2017 Reviewed: January 12th, 2018 Published: June 27th, 2018

DOI: 10.5772/intechopen.73879

From the Edited Volume

Heavy Metals

Edited by Hosam El-Din M. Saleh and Refaat F. Aglan

Chapter metrics overview

1,782 Chapter Downloads

View Full Metrics


The continued accumulation of trace and heavy metals in the environment presents a significant danger to biota health, including humans, which is undoubtedly undermining global environmental sustainability initiatives. Consequently, the need for efficient remediation technologies becomes imperative. Phytoremediation is one of the most viable options in this regard. Hundreds of plants in laboratory experiments demonstrate the potential to remediate varying concentrations of heavy metals; however, the remediation capacity of most of these plants proved unsatisfactory under field conditions. The identification and selection of plants with higher metal uptake capacity or hyperaccumulators are one of the limitations of this technology. Additionally, the mechanism of heavy metal uptake by plants remains to be sufficiently documented. The halophyte plants are famous for their adaptation to harsh environmental conditions, and hence could be the most suitable candidates for heavy metal hyperaccumulation. The state of Qatar in the Gulf region encompasses rich resources of halophytes that have the potential for future investment toward human and environmental health. This chapter, therefore, gives an overview of phytoremediation, with emphasis on halophytes as suitable heavy metal hyperaccumulators for improved remediation of heavy metal–contaminated areas.


  • halophytes
  • phytoremediation
  • heavy metals
  • hyperaccumulation

1. Introduction

Heavy metals and other organic compounds constitutes the major environmental contaminants, and the trials of phytoremediation to free pollutants from waste water and contaminated soil dates back to hundreds of years ago in plants such as the Thlaspi caerulescens and Viola calaminaria, which were reported to remediate high concentration of heavy metals [1]. Anthropogenic activities arising from industrialization largely contribute to the proliferation of these contaminants, either by direct leakage or accidents during transport of solid and liquid wastes from storage and industrial facilities [2, 3]. Strategies to clean up environmental contaminants, both organic and inorganic are either by physical, chemical and or biological treatments [4, 5]. However, physical and chemical methods are recognized for a number of disadvantages or limitations such as high cost and labor intensiveness. Additionally, chemical processes create another pollution and are especially costly since they generate heaps of sludge [6]. In view of this context, new and better approaches to clean up of metal contamination were thought up and became imperative, hence the exploration of various bio-based techniques. The use of biological agents is considered cheap, safer and has limited or no negative impact to the environment [7]. Bio-based remediation methods include bio-augmentation, bioremediation, bioventing, composting and phytoremediation. However, phytoremediation proves the most viable and useful alternative and has gain an increasing attention in recent times [8, 9]. The adverse and negative effects associated with these elements make them targets for phytoremediation [10]. Phytoremediation offer several advantages. It is cheap, promotes biodiversity, reduces erosion, less destructive and decreased energy consumption leading to reduced carbon dioxide emission [11]. To date, about 400 plant species were suggested to be metal hyper-accumulators [12]. However, few studies reported the toxicity of several metals combined [13], and while hyper-accumulation of nickel (Ni), cadmium (Cd), manganese (Mn), zinc (Zn) and selenium (Se) have been well established, the same is yet be available or demonstrated beyond doubt in plant species for copper (Cu), chromium (Cr), lead (Pb), thallium (Th) and cobalt (Co) metals. For instance, Cu is an important element for growth and general plant physiology, owing to its role as a cofactor to various types of enzymes involved in the transfer of electrons during metabolic processes, such as the tricarboxylic acid (TCA) cycle [14, 15]. However, at high concentrations, it is toxic to plants signaled by stunted growth, and although there is some physiological insight to Cu stress in plants, the responses are still vague at the functional level [16]. The accumulation of heavy metals in plant tissues results in a wide range of negative effects on growth. Although it affects seed germination, growth of seedlings and photosynthetic processes, which generally leads to the inhibition of the plants important enzymatic activity [17, 18], however, plants responds differently [19]. In dealing with the heavy metal stress, the root tissue is the first to be exposed to the associated toxins, and its cell wall has a mechanism of exchange that fixes the heavy metal ions, thereby limiting the transmission of the toxins to other plant tissues [20, 21]. Several studies reported many plants, including desert species as good phytoremediation agents, however, few are metal hyperaccumulators and their selection for efficient phytoremediation is still a challenge. This is demonstrated by slow growth, above ground biomass, root system and harvest [22]. Accordingly, successful heavy metal phytoremediation requirement of hyperaccumulation capacity in candidate plants position halophytes as suitable phytoremediators. This is due to their extensive stress tolerance mechanism, which enables them thrive in saline soil and in other desert conditions.


2. Phytoremediation

In simple terms, phytoremediation refers to a process where plants are employed to reduce or free up organic and inorganic contaminants from the environment [13] with the aid of associated microbes. The process by which contaminants are remediated differs; these may be in the form of removal, transfer, degradation and immobilization from either soil or water [23]. It is a unique approach capitalizing on plants roots ability for the initial uptake of pollutants, and eventually accumulating them onto the shoot tissue by translocation across the stem. Compared to other conventional treatment techniques, phytoremediation is new, with a great potential to providing the much-needed green technology solution to our deteriorating environment. To date, hundreds of plant species were suggested as potential phytoremediation agents [24].

2.1. Phytoremediation techniques

During phytoremediation, plants growing on soil or water contaminated with trace or heavy metals could absorb or tolerate these elements differently, depending on the physiological means involved and the kinds of metals present [25]. According to Halder and Ghosh [26] phytoremediation techniques are categorized into five; phytoextraction, phytofiltration, phytovolatilization, phytostabilization and phytotransformation.

2.1.1. Phytoextraction

Phytoextraction is a technique of phytoremediation where plants take up metals by translocation, and accumulate them in a form that can be extracted on its tissue [27]. It is one of the most common types of phytoremediation and the names; phytoabsorption, phytoaccumulation and phytosequestration are often used interchangeably to refer to phytoextraction [28]. It is considered as the major phytoremediation technique among all others for the removal of metals from contaminated water, sediment and soil. The efficiency of this remediation process depends on a number of factors from soil properties, metal bioavailability and speciation to the type of plant species. However, high concentration of absorbed metals usually ends up in the shoot biomass of the plant in harvestable form [12]. A number of recent studies reported various plant species that demonstrate phytoextraction strategy from both water and soil media [29, 30, 31, 32].

Plants able to exhibit phytoextraction strategy in metal sequestration may potentially be hyper accumulators, referring to plants that consistently accumulate certain threshold of metal concentration in their shoot tissue, which varies according to the metals [22]. Generally, all hyper accumulators should possess characteristics such as high growth rate, widely branched shoot, high bioaccumulation and translocation capacity, high above ground biomass, easily cultivated and harvested [22, 33]. However, Ali, Khan [28] demonstrated two methods or approaches for metal phytoextraction in different plants, one producing less above ground biomass but significantly accumulate metals in high concentration and vice versa in the other plant species, with final metal accumulation in agreement with those of hyper accumulators. Consequently, hyper accumulation is more important in phytoremediation than volume of biomass produced, and this suggest the use of hyper accumulators as more acceptable since it has advantages such as safe disposal, cheap process and easy handling [28].

2.1.2. Phytofiltration

Phytofiltration or rhizofiltration, as used interchangeably, refers to the absorption or adsorption of contaminants from surface wastewater by plant roots thereby preventing them from leaching to the underground water [34]. It is a type of phytoremediation technique that can be demonstrated in situ by directly growing plants in the polluted water body [24]. Although it is commonly applicable using aquatic plant species [35], there are suggestions that the process may be applied to terrestrial plants, which remediate metals to precipitate with the aid of microbes root bio filter [36]. Indeed, root exudates cause metal precipitation which alters the rhizosphere pH level [37]. Many terrestrial plants including grasses grown in a hydroponic culture were shown to effectively remove metals such via phytofiltration [38]. In the same study, Indian mustard was especially reported to accumulate higher fold of metal concentration far beyond the initial concentration, and the removal is by tissue specific adsorption mediated by root metal concentration.

Quite a number of studies have shown many species of aquatic macrophytes that demonstrate phytofiltration potential. While experimenting for phytoremediation under different water conditions polluted with heavy metals, Liao and Chang [39] found that Eichhonia crassipes absorb and accumulates metal contaminants, it has also exhibit high growth rate and increased biomass production and thus considered a good phytofiltration agent. This plant species absorb high concentrations of Pb, Ni, Zn and Cu which accumulates much higher in the root tissue than the shoot, suggesting the important role of fibrous and tap root system found in the plant, which is one of the key characteristics of potential phytofiltration agent. In a similar study, other aquatic plant species including Salvinia herzogii, E. crassipes, Pistia stratiotes and Hydromistia stolonifera were shown to absorb high concentration of Cd with P. stratiotes accumulating higher Cd concentration and exhibiting faster growth rate, a feature attributed to possible complimentary mechanism for the enhanced metal uptake [40]. Absorption of Cd in the root of all the plants relates to the added concentration. In another study by Thayaparan, Iqbal [41] also reported that Azolla pinnata have shown a great potential in the removal of high Pb concentration by phytofiltration from polluted water. As in phytoextraction, potential phytofiltration agents should tolerate high metal concentration, exhibit fast and high growth rate as well as above ground biomass, however, in contrast to phytoextraction, they are expected to show limited translocation capacity of absorbed metals from root to shoot tissues [24]. For efficient phytofiltration, this is an advantage over phytoextraction, since low translocation of contaminants means reduced contamination of other parts of the plant.

2.1.3. Phytostabilization

In this technique, pollutants are converted into a less toxic or bioavailable form by the continuous precipitation of the plant rhizosphere. This is achieved either by surface run off prevention, erosion or leaching [27]. It is applicable in the stabilization of metals in contaminated soil, sediment or water environments, which ensures they are not transferred to the food chain from the soil by translocating to other parts of food crops or to the underground water. This is possible by sorption via the root, precipitation and subsequent metal reduction around the plant rhizosphere, for instance the toxic Cr6+ is converted to Cr3+, which is less toxic [42, 43]. Variation exists as to how prone a metal is to phytostabilization and is subject to its chemical character. This is evidenced in a comparative study to evaluate metal accumulation capacity of two aquatic macrophytes Phragmites australis and Typha domingensis, where both are found to stabilize As and Hg but inefficient in the phytostabilization of other metals [44].

Although phytostabilization offer some advantages over other phytoremediation techniques, it is however limited to temporary measure to deal with pollutants contamination owing to the fact that metals are only inactivated and their movement restricted, but still remains in the contaminated environmental compartment [45]. It is useful in emergencies, since it can rapidly immobilize pollutants from soil, water or sediment. Equally important, it ensures that contaminants are not translocated to other plant tissues by trapping most of it in the plant root [46]. Considering the strategies employed in phytostabilization, plants that can appropriately fall under this mechanism is their ability to tolerate and immobilize metals and other contaminants, low translocation capacity from root to plant aerial parts and of course extensive and fibrous tap root system [7]. Among several studies that reported plants species with these characteristics [47, 48, 49] demonstrating the phytostabilization of Zn, Pb, Cu and Cd by different plants in soil and sediment polluted environments.

2.1.4. Phytotransformation/phytodegradation

Phytotransformation or phytodegradation is another technique of phytoremediation where contaminants and other nutrients are chemically modified through plant metabolism and render associated contaminants inactive in both plant root and shoot tissues [6]. Plant metabolic enzymes act on the surrounding contaminants, thereby transforming them to a less toxic form, plants rhizosphere microbes also aid in the transformation process of the compounds [50]. Although this mechanism is mostly against organic contaminants, inorganic compounds such as metals were also suggested, in which case a strategy akin to phytostabilization is employed to convert toxic metals to less toxic form [51]. However, this technique seem less efficient and reliable compared to others in that it requires longer period of time, strict soil characteristic such as depth and underground water availability and often require soil amendments.

2.1.5. Phytovolatilization

In phytovolatilization, contaminants are converted in to a volatile form and released to the air via plants leaves stomata [27, 34]. However, this mechanism merely transfers contaminants from one environmental compartment to another, which may somehow return back to the original source (soil) by precipitation and hence could be less popular to other phytoremediation techniques especially phytoextraction and phytofiltration [34, 52]. It is commonly employed when treating groups of highly volatile metals like Hg and As. Phytovolatilization of As involves the conversion of elemental As to selenoaminoacids, such as selenomethione, which is modified by methylation to a volatile and less toxic form, dimethylselenide [53].


3. Metal hyperaccumulator plants

Several plants species are known to tolerate high concentration of toxic metals. Tolerant species are best described as excluders, where metal uptake and translocation to different tissue parts are limited. While others that are capable of accumulating higher concentrations with improved translocation from the root to shoot part of the plant, thereby significantly reducing its availability in the soil, and they do so with no visible sign of toxicity effects. To date, heavy metals have no standard definition by recognized bodies in the area. Various researchers use different characteristics and levels in their description such as atomic mass and number, density, chemical character as well as their toxicity; however, there appears no connection between such properties [54]. According to Wang and Chen [55], three categories of heavy metals arising from both natural and artificial sources are of interest, these includes valuable metals e.g. Ag, Au, Pd, Pt, harmful metals e.g., As, Cu, Co, Cd, Cr, Hg, Ni, Pb, and radionuclides such as Am, Th, Ra and so on. The non-biodegradability and stable nature of heavy metals suggests increased exposure to living species including humans [54], periodic reviews of toxic metals effects are documented by many research groups [56, 57, 58].

When determining hyperaccumulators of toxic metal, the most important factor is the concentration of the metal ion threshold. Therefore, plants can be regarded as hyperaccumulators, when capable of accumulating toxic metals concentration to about 50 to 100 times more than non-hyperaccumulator plants [13, 59]. For instance, the threshold for Zn and Mn hyperaccumulation in plant shoot is pegged at 1% of dry biomass, 0.01% for Cd and 0.1% respectively for Ti, Se, Sb, Pb, Ni, Cu, Cr, Co, and As [13, 60]. To date, few plant species are classified as hyperaccumulators, the majority of them (3/4) are tolerant to Ni and belongs to the Brassicaceae family native to Western Asia and Southern Europe, with up to 48 species implicated in Ni accumulation of around 3% dry shoot mass [60, 61, 62]. There is increasing interest in plant hyperaccumulators in recent times, owing to their potential use in metal contaminated soil and water detoxification [25, 63].

3.1. The role of metal chelators in hyperaccumulation

The phytoremediation of heavy metals involve many physiological, biochemical and molecular activities. In this process, especially phytoextraction involves the accumulation and translocation of heavy metals to plant tissues. Plant metal chelators or phytochelatins (PCs) and metallothioneins (MTs) are the most common transporter proteins for heavy metal phytoremediation. MTs are cysteine rich proteins that are famous for metal binding and greatly assist in the process of sequestration of metals in ionic form [64]. PCs are glutathione synthase products and they binds to heavy metals thereby forming central part of the phyto-detoxification mechanism [65, 66]. The induction of phytochelatins is induced by the activity of an enzyme, phytochelatins synthase, which is triggered by the activity of metal ions present [34, 67]. In an experiment to demonstrate the role of synthases, mutants in model plant Arabidopsis thaliana were shown to be hypersensitive to Hg and Cd, which is attributed to their inability to produce PCs [68]. On the other hand, MTs are genetically encoded metal binding peptides and usually bear low molecular weight. A number of studies demonstrate MTs role in the protection of plants against the toxicity of heavy metals in soil, sediment and water [65, 69, 70]. The expression of MTs and PCs, alongside organic acid synthesis, together functions in heavy metal uptake by plants and also their translocation to other tissue parts [42]. The expression of these natural chelators could be enhanced to increase the efficiency of heavy metal accumulation and translocation. Currently, there are many ongoing studies aimed at characterizing and identifying biomolecules involved in the transport and detoxification of heavy metals. This will aid in understanding the whole detoxification process involved in plants [28, 71], and to achieve this, the importance of comparative proteomic studies cannot be over-emphasized.

3.1.1. The shoot proteome

Plant shoot is an important tissue in phytoremediation process; it is especially responsible for accumulating the highest metals concentration when the subject plant employs phytoextraction technique, which is subject to the type of metal elements and bioavailability. In recent times, there has been an increased interest in the proteomics study of plant hyperaccumulators with the aim of characterizing and identifying proteins acting in metal sequestration and detoxification [72]. These are possible with the advancement in modern mass spectrometry techniques such as two-dimensional liquid chromatography matrix-assisted laser desorption/ionization time-of-flight (2D-LC/TOFMS), time of flight/mass spectrometry (TOF/MS), two-dimensional polyacrylamide gel electrophoresis (2D PAGE), and liquid chromatography- tandem mass spectrometry (LC–MS/MS). For instance, the proteome of many plants species including Thlaspi caerulescens, Pteris vittata, Helianthus annuus and Agrostis tenuis were recently searched for heavy metals detoxifying proteins; several key functional proteins were found that protect plants against oxidative stress, as well as those responsive to biotic and abiotic stress condition among others [12, 73, 74].

In the proteomics study of plant metal hyperaccumulators, comparison could be made, even when these studies are from different plants and metals. In 2005, [75] found that prolonged exposure of Alyssum lesbiacum to Ni in an optimized experimental condition induced only three proteins, and one of these proteins, iron superoxide dismutase (Fe-SOD), was demonstrated to have antioxidant activity [76], while the other two proteins were identified as chloroplast phosphoglycerate kinase and a transketolase both having a role in the carbohydrates metabolism. In Anemone halleri, photosynthetic protein (chlorophyll a/b binding) and membrane protein (photosystem II) were constantly translated and upregulated when treated with Zn and Cd, which is linked to the improved metabolic energy demand in this metal hyperaccumulating plant [77].

At high metal concentrations, increased proteins induction are involved in the defense against antioxidants and energy metabolism has been consistently observed; examples includes Renal Epithelial Protein (APX), Superoxide dismutase (SOD), cytochrome P450 and Glutathione S-transferase (GST). These suggest that, for the uptake, translocation and accumulation of heavy metals concentration on the shoot tissue, plants require the functional photosynthetic process as well as the activity of proteins that scavenge oxygen radical species [13]. Metabolic energy active proteins were also suggested to have important roles in metal tolerance by plants. The proteomes of T. caerulescens with variable tolerance to Cd and Zn metals were compared and there was a higher accumulation of the extrinsic subunit of photosystem II protein, which led to its stabilization in the more metal tolerant variant as against the less tolerant accession. In addition to GST and cytochrome P450 earlier mentioned, other proteins such as aspartate aminotransferase and thioredoxin are commonly found, and linked to the sequestration of xenobiotics including metals. GSTs have particularly been demonstrated to be up regulated in many other living species including bacteria and fungi treated with metals like Zn, Cu and Cd [78]; hence GST were suggested to confer resistance to toxic genes in these cells.

3.1.2. The root proteome

In plants, the root tissue is the first to be exposed to all potential toxicants whether in the soil or surface water and hence serve as the gateway route through which they can subsequently be translocated to other tissue parts. Plants diversity as to hyperaccumulators and non-hyperaccumulators exist, this is due to the fact that, while some species bear the complete mechanism of enhanced metal uptake and eventual translocation, others have limited sequestration capacity in their root vacuoles [79]. In non-hyperaccumulators plant roots, Zn transporters are only detectable in the absence of Zn, whereas in hyperaccumulators, there is constitutive expression of these proteins such as ZT1 even in Zn deficient condition [80, 81]. In T. caerulescens, the iron transporter protein IRT1 was found to be involved in Zn and Cd uptake [82], similarly, root proteome study of this hyperaccumulator and A. lesbiacum were conducted by Tuomainen, Tervahauta [83] to evaluate peptides involved in Zn and Cd hyperaccumulation. In these studies, various classes of proteins were identified, their availability and or abundance varies relative to metal exposure and accessions. As in the case with similar studies on shoot proteome of hyperaccumulators, ROS scavenging proteins were more abundant in the more metal tolerant accessions compared to the less metal tolerant species. It was concluded that the changes in the enzyme, superoxide dismutase (SOD) availability upon which Zn depends in the different accessions may be linked to ROS increase.

An important organelle, cell wall, in the plant root is also affected by its exposure to heavy metal stress. The putative protein, glycosyl hydrolase family 18, involved in the formation of cell wall structure was shown to be regulated in accordance to treatment conditions and accession. These proteins, which are particularly known to be involved in cell wall expansion, differ in terms of abundance between the root proteome of two accessions, which in turn also affect the capacity of metals uptake; higher Ni and Cd accumulation was observed in the variant with more protein abundance [13]. Despite the recent advancement in proteomics technology, root protein transporters are yet to be differentially identified. Indeed, this is in agreement with transcriptomics studies, with analyzed data suggesting the constitutive expression of metal genes transporters in plant metal hyperaccumulators [13, 81, 84].

3.2. The halophytes of Qatar are promising heavy metal hyperaccumulators

Some studies demonstrated the potential of several Qatari plants as good phytoremediation candidates, many among which are heavy metal hyperaccumulators. Examples includes species belonging to the genus Zygophyllum, which are as either metal tolerant or accumulators when tested on both polluted soil and wastewater media [85, 86, 87, 88, 89]. Others include Typha domingensis and Phragmites australis [2]. According to Carvalho and Martin [90], Typha domingensis remediated heavy metals from industrial waste water and solution cultures; similarly, members of the halophytes plant family Brassicaceae were reported to be important phytoremediation agents [3, 59, 91] and the tree plant Prosopis juliflora exhibited phytoremediation of heavy metals potential [92, 93]. Additionally, such as other plants, such as Phragmites australis that were previously shown to clean petroleum-polluted soils may be good candidates for the phytoremediation of typical oil and gas produced wastewater [94], others with similar potentials includes Medicago such as Medicago sativa and Glycine max which also demonstrated strong petroleum polluted soil phytoremediation activity [95, 96]. Some examples of other species tested for phytoremediation studies and their metal uptake capacity are summarized in Table 1 above.

S/No Plant species Metal (s) Metal accumulation (mg/kg) References
1 Atriplex halimus subsp. schweinfurthii Cadmium 606.51 [97]
A. halimus L. Cadmium 830 [98]
Zinc 44
2 Arthrocnemum macrostachyum Lead 620 [99]
3 Crucianella maritima Zinc 390 [99]
4 Dittrichia viscosa Lead 270 [99]
5 Tamarix smyrnensis Bunge Lead 800 [100]
Cadmium 800
6 Typha domingensis Selenium 30 [90]
Lead 59.13 [101]
7 T. lotifolia L Cadmium 210 [102]
8 Paspalum conjugatum L.
Prosopis laevigata
Lead 150 [103]

Table 1.

Examples of phytoremediation studies using species belong to Qatari flora and/or their relatives.


4. Conclusion

The accumulation of trace and heavy metals in the environment present a great risk to biota health. These contaminants are implicated in a wide range of human diseases and various long-term negative environmental consequences, thereby endangering overall sustainable development initiatives worldwide. Many conventional treatment strategies are widely practiced for the remediation of these contaminants. However, traditional remediation processes have many disadvantages, from complicating environmental pollution to high operational cost among others. Phytoremediation is one of the most promising alternatives in this regard, and laboratory experiments have demonstrated the capacity of hundreds of plants species to remediate different heavy metal contaminants. However, there still exist limitations in the application of this emerging technology. This may be linked to exposure to other stress factors in field conditions, and especially in extreme environments, which could significantly affect physiological function and general growth. An example is above the ground biomass accumulation, a key requirement for plants that is critical to phytoremediation success. The identification and selection of plants with higher metal uptake capacity or hyperaccumulators, even in the presence of other stress condition is therefore the objective of many phytoremediation studies in recent times. Additionally, our limited understanding on the molecular mechanism of heavy metal remediation, such as the exact role of transporter proteins is compounding progress in this area. However, it is obvious that several stress response molecules are key to the tolerance and or accumulation of heavy metal contaminants by potential phytoremediators. The halophytes are famous for their adaptation to stress environmental conditions, and hence could be the most suitable candidates in the search for appropriate heavy metal hyperaccumulators and consequent elucidation of mechanism of uptake. Indeed, these are significant steps essential to improving the efficiency of phytoremediation for large scale, field and industrial applications.



This book chapter was financially supported for publication by Qatar National Library (a member of The Qatar Foundation). The statements made herein are solely the responsibility of the authors. The authors wish to acknowledge the funding support of Academic Research Office at Qatar University for the grant (QUST-CAS-SPR-2017-2033).


Conflict of interest

The authors wish to declare no conflict of interest.


  1. 1. Lasat MM. Phytoextraction of toxic metals. Journal of Environmental Quality. 2002;31(1):109-120
  2. 2. Yasseen BT, Al-Thani RF. Ecophysiology of wild plants and conservation perspectives in the State of Qatar. In: Stoytcheva M, Zlatev R, editor. Agricultural Chemistry. Croatia: InTech; 2013. pp. 210. ISBN: 978-953-51-1026-2
  3. 3. Lone MI et al. Phytoremediation of heavy metal polluted soils and water: Progresses and perspectives. Journal of Zhejiang University. Science. B. 2008;9(3):210-220
  4. 4. Baldwin SA et al. The microbial community of a passive biochemical reactor treating arsenic, zinc, and sulfate-rich seepage. Frontiers in Bioengineering and Biotechnology. 2015;3:27
  5. 5. Hasegawa H, Rahman IMM, Rahman MA, editors. Environmental Remediation Technologies for Metal-Contaminated Soils. Tokyo: Springer; 2016. 254 p. DOI: 10.1007/978-4-431-55759-3.
  6. 6. Tangahu BV et al. A review on heavy metals (As, Pb, and Hg) uptake by plants through phytoremediation. International Journal of Chemical Engineering. 2011;2011:31. DOI:10.1155/2011/939161
  7. 7. Doble M, Kumar A. Biotreatment of Industrial Effluents. Oxford: Elsevier; 2005. 336 p
  8. 8. Witters N. Phytoremediation: An alternative remediation technology and a sustainable marginal land management option [Thesis]. Hasselt: Hasselt University; 2011
  9. 9. Ullah A et al. Phytoremediation of heavy metals assisted by plant growth promoting (PGP) bacteria: A review. Environmental and Experimental Botany. 2015;117:28-40
  10. 10. Monica RC, Cremonini R. Nanoparticles and higher plants. Caryologia. 2009;62(2):161-165
  11. 11. Ali-Zade V, Alirzayeva E, Shirvani T. Plant resistance to anthropogenic toxicants: Approaches to phytoremediation. In: Plant Adaptation and Phytoremediation. Netherlands: Springer; 2010. pp. 173-192
  12. 12. Walliwalagedara C et al. Differential expression of proteins induced by lead in the dwarf sunflower Helianthus annuus. Phytochemistry. 2010;71(13):1460-1465
  13. 13. Visioli G, Marmiroli N. The proteomics of heavy metal hyperaccumulation by plants. Journal of Proteomics. 2013;79:133-145
  14. 14. Himelblau E, Amasino RM. Delivering copper within plant cells. Current Opinion in Plant Biology. 2000;3(3):205-210
  15. 15. Hall J. Cellular mechanisms for heavy metal detoxification and tolerance. Journal of Experimental Botany. 2002;53(366):1-11
  16. 16. Lin C-Y et al. Comparison of early transcriptome responses to copper and cadmium in rice roots. Plant Molecular Biology. 2013;81(4-5):507-522
  17. 17. Singh RP et al. Response of higher plants to lead contaminated environment. Chemosphere. 1997;34(11):2467-2493
  18. 18. Sharma P, Dubey RS. Lead toxicity in plants. Brazilian Journal of Plant Physiology. 2005;17(1):35-52
  19. 19. Liu D et al. Uptake and accumulation of lead by roots, hypocotyls and shoots of Indian mustard [Brassica juncea (L.)]. Bioresource Technology. 2000;71(3):273-277
  20. 20. Allan DL, Jarrell WM. Proton and copper adsorption to maize and soybean root cell walls. Plant Physiology. 1989;89(3):823-832
  21. 21. Branquinho C, Brown DH, Catarino F. The cellular location of Cu in lichens and its effects on membrane integrity and chlorophyll fluorescence. Environmental and Experimental Botany. 1997;38(2):165-179
  22. 22. van der Ent A, et al., Hyperaccumulators of metal and metalloid trace elements: Facts and fiction. Plant and Soil, 2013. 362(1-2): p. 319-334
  23. 23. Ahmadpour P et al. Phytoremediation of heavy metals: A green technology. African Journal of Biotechnology. 2012;11(76):14036-14043
  24. 24. da Conceição Gomes MA et al. Metal phytoremediation: General strategies, genetically modified plants and applications in metal nanoparticle contamination. Ecotoxicology and Environmental Safety. 2016;134:133-147
  25. 25. Pilon-Smits EA, Freeman JL. Environmental cleanup using plants: Biotechnological advances and ecological considerations. Frontiers in Ecology and the Environment. 2006;4(4):203-210
  26. 26. Halder S, Ghosh S. Wetland macrophytes in purification of water. International Journal of Environmental Sciences. 2014;5(2):432-437
  27. 27. Nwoko CO. Trends in phytoremediation of toxic elemental and organic pollutants. African Journal of Biotechnology. 2010;9(37):6010-6016
  28. 28. Ali H, Khan E, Sajad MA. Phytoremediation of heavy metals—Concepts and applications. Chemosphere. 2013;91(7):869-881
  29. 29. Li J et al. Cadmium tolerance and accumulation in cultivars of a high-biomass tropical tree () and its potential for phytoextraction. Journal of Environmental Quality. 2010;39(4):1262-1268
  30. 30. Simmons R et al. Towards practical cadmium phytoextraction with Noccaea caerulescens. International Journal of Phytoremediation. 2015;17(2):191-199
  31. 31. Kacálková L, Tlustoš P, Száková J. Phytoextraction of risk elements by willow and poplar trees. International Journal of Phytoremediation. 2015;17(5):414-421
  32. 32. Shaheen SM, Rinklebe J. Phytoextraction of potentially toxic elements by Indian mustard, rapeseed, and sunflower from a contaminated riparian soil. Environmental Geochemistry and Health. 2015;37(6):953-967
  33. 33. Sharma P, Pandey S. Status of phytoremediation in world scenario. International Journal of Environmental Bioremediation & Biodegradation. 2014;2(4):178-191
  34. 34. Sarma H. Metal hyperaccumulation in plants: A review focusing on phytoremediation technology. Journal of Environmental Science and Technology. 2011;4(2):118-138
  35. 35. Olguín EJ, Sánchez-Galván G. Heavy metal removal in phytofiltration and phycoremediation: The need to differentiate between bioadsorption and bioaccumulation. New Biotechnology. 2012;30(1):3-8
  36. 36. Salt DE et al. Phytoremediation: A novel strategy for the removal of toxic metals from the environment using plants. Nature Biotechnology. 1995;13(5):468-474
  37. 37. Rai PK. Heavy metal pollution in aquatic ecosystems and its phytoremediation using wetland plants: An ecosustainable approach. International Journal of Phytoremediation. 2008;10(2):133-160
  38. 38. Khilji S. Rhizofiltration of heavy metals from the tannery sludge by the anchored hydrophyte, Hydrocotyle umbellata L. African Journal of Biotechnology. 2008;7(20)
  39. 39. Liao S, Chang W-L. Heavy metal phytoremediation by water hyacinth at constructed wetlands in Taiwan. Photogrammetric Engineering and Remote Sensing. 2004;54:177-185
  40. 40. Maine MA, Duarte MV, Suñé NL. Cadmium uptake by floating macrophytes. Water Research. 2001;35(11):2629-2634
  41. 41. Thayaparan M et al. Rhizofiltration of Pb by Azolla Pinnata. International Journal of Environmental Sciences. 2013;3(6):1811
  42. 42. Wu G et al. A critical review on the bio-removal of hazardous heavy metals from contaminated soils: Issues, progress, eco-environmental concerns and opportunities. Journal of Hazardous Materials. 2010;174(1):1-8
  43. 43. Ghosh M, Singh S. A review on phytoremediation of heavy metals and utilization of it’s by products. Asian Journal on Energy & Environment. 2005;6(4):18
  44. 44. Bonanno G. Comparative performance of trace element bioaccumulation and biomonitoring in the plant species Typha domingensis, Phragmites australis and Arundo donax. Ecotoxicology and Environmental Safety. 2013;97:124-130
  45. 45. Vangronsveld J et al. Phytoremediation of contaminated soils and groundwater: Lessons from the field. Environmental Science and Pollution Research. 2009;16(7):765-794
  46. 46. Abreu CA et al. Organic matter and barium absorption by plant species grown in an area polluted with scrap metal residue. Applied and Environmental Soil Science. 2012;2012
  47. 47. Andreazza R et al. Evaluation of two Brazilian indigenous plants for phytostabilization and phytoremediation of copper-contaminated soils. Brazilian Journal of Biology. 2015;75(4):868-877
  48. 48. Najeeb U et al. Enhancing the lead phytostabilization in wetland plant Juncus effusus L. through somaclonal manipulation and EDTA enrichment. Arabian Journal of Chemistry. 2014
  49. 49. Zhang X, Zhang X, Huang K. Phytostabilization of acidic soils with heavy metal contamination using three forage grasses in combination with organic and inorganic amendments. Soil and Sediment Contamination: An International Journal, 2016(just-accepted): p. 00-00
  50. 50. Dobos L, Carmen P. The most important methods for depollution of hydrocarbons polluted soils. Bulletin of University of Agricultural Sciences and Veterinary medicine Cluj-Napoca Agriculture. 2009;66(1)
  51. 51. Kobraee S et al. Influence of micronutrient fertilizer on soybean nutrient composition. Indian Journal of Science and Technology. 2011;4(7):763-769
  52. 52. Nikolić M, Stevović S. Family Asteraceae as a sustainable planning tool in phytoremediation and its relevance in urban areas. Urban Forestry & Urban Greening. 2015;14(4):782-789
  53. 53. Wang J et al. Remediation of mercury contaminated sites–a review. Journal of Hazardous Materials. 2012;221:1-18
  54. 54. Sathya A et al. Cultivation of sweet sorghum on heavy metal contaminated soils by phytoremediation approach for production of bioethanol. In: Bioremediation and Bioeconomy. 2016. pp. 271-292
  55. 55. Wang J, Chen C. Biosorption of heavy metals by Saccharomyces cerevisiae: A review. Biotechnology Advances. 2006;24(5):427-451
  56. 56. Wongsasuluk P et al. Heavy metal contamination and human health risk assessment in drinking water from shallow groundwater wells in an agricultural area in Ubon Ratchathani province, Thailand. Environmental Geochemistry and Health. 2014;36(1):169-182
  57. 57. Duruibe J, Ogwuegbu M, Egwurugwu J. Heavy metal pollution and human biotoxic effects. International Journal of Physical Sciences. 2007;2(5):112-118
  58. 58. Nagajyoti P, Lee K, Sreekanth T. Heavy metals, occurrence and toxicity for plants: A review. Environmental Chemistry Letters. 2010;8(3):199-216
  59. 59. Baker A, Brooks R. Terrestrial higher plants which hyperaccumulate metallic elements. A review of their distribution, ecology and phytochemistry. Biorecovery. 1989;1(2):81-126
  60. 60. Krämer U. Metal hyperaccumulation in plants. Annual Review of Plant Biology. 2010;61:517-534
  61. 61. Milner MJ, Kochian LV. Investigating heavy-metal hyperaccumulation using Thlaspi caerulescens as a model system. Annals of Botany. 2008;102(1):3-13
  62. 62. Baker AJ et al. Metallophytes: The unique biological resource, its ecology and conservational status in Europe, central Africa and Latin America. Ecology of Industrial Pollution. 2010:7-40
  63. 63. Chaney RL et al. Improved understanding of hyperaccumulation yields commercial phytoextraction and phytomining technologies. Journal of Environmental Quality. 2007;36(5):1429-1443
  64. 64. Kärenlampi S et al. Genetic engineering in the improvement of plants for phytoremediation of metal polluted soils. Environmental Pollution. 2000;107(2):225-231
  65. 65. Fulekar M, Singh A, Bhaduri AM. Genetic engineering strategies for enhancing phytoremediation of heavy metals. African Journal of Biotechnology. 2009;8(4)
  66. 66. Yurekli F, Kucukbay Z. Synthesis of phytochelatins in Helianthus annuus is enhanced by cadmium nitrate. Acta Botanica Croatica. 2003;62(1):21-25
  67. 67. Cobbett CS. Phytochelatin biosynthesis and function in heavy-metal detoxification. Current Opinion in Plant Biology. 2000;3(3):211-216
  68. 68. Memon AR, Schröder P. Implications of metal accumulation mechanisms to phytoremediation. Environmental Science and Pollution Research. 2009;16(2):162-175
  69. 69. Jabeen R, Ahmad A, Iqbal M. Phytoremediation of heavy metals: Physiological and molecular mechanisms. The Botanical Review. 2009;75(4):339-364
  70. 70. Sheoran V, Sheoran A, Poonia P. Role of hyperaccumulators in phytoextraction of metals from contaminated mining sites: A review. Critical Reviews in Environmental Science and Technology. 2010;41(2):168-214
  71. 71. Seth CS. A review on mechanisms of plant tolerance and role of transgenic plants in environmental clean-up. The Botanical Review. 2012;78(1):32-62
  72. 72. Visioli G, Marmiroli N. Proteomics of plant hyperaccumulators. In: Metal Toxicity in Plants: Perception, Signaling and Remediation. Berlin, Heidelberg: Springer; 2012. pp. 165-186
  73. 73. Bona E et al. Proteomic analysis of Pteris vittata fronds: Two arbuscular mycorrhizal fungi differentially modulate protein expression under arsenic contamination. Proteomics. 2010;10(21):3811-3834
  74. 74. Visioli G et al. Comparison of protein variations in Thlaspi Caerulescens populations from metalliferous and non-metalliferous soils. International Journal of Phytoremediation. 2010;12(8):805-819
  75. 75. Ingle RA, Smith JAC, Sweetlove LJ. Responses to nickel in the proteome of the hyperaccumulator plant alyssum lesbiacum. BioMetals. 2005;18(6):627-641
  76. 76. Freeman JL et al. Increased glutathione biosynthesis plays a role in nickel tolerance in Thlaspi nickel hyperaccumulators. The Plant Cell. 2004;16(8):2176-2191
  77. 77. Farinati S et al. Proteomic analysis of Arabidopsis halleri shoots in response to the heavy metals cadmium and zinc and rhizosphere microorganisms. Proteomics. 2009;9(21):4837-4850
  78. 78. Waschke A et al. Identification of heavy metal-induced genes encoding glutathione S-transferases in the arbuscular mycorrhizal fungus Glomus intraradices. Mycorrhiza. 2006;17(1):1-10
  79. 79. Maestri E et al. Metal tolerance and hyperaccumulation: Costs and trade-offs between traits and environment. Environmental and Experimental Botany. 2010;68(1):1-13
  80. 80. Pence NS et al. The molecular physiology of heavy metal transport in the Zn/Cd hyperaccumulator Thlaspi caerulescens. Proceedings of the National Academy of Sciences. 2000;97(9):4956-4960
  81. 81. Assunção A et al. Elevated expression of metal transporter genes in three accessions of the metal hyperaccumulator Thlaspi caerulescens. Plant, Cell & Environment. 2001;24(2):217-226
  82. 82. Lombi E et al. Influence of iron status on cadmium and zinc uptake by different ecotypes of the hyperaccumulator Thlaspi caerulescens. Plant Physiology. 2002;128(4):1359-1367
  83. 83. Tuomainen M et al. Proteomics of Thlaspi caerulescens accessions and an inter-accession cross segregating for zinc accumulation. Journal of Experimental Botany. 2010;61(4):1075-1087
  84. 84. Hammond JP et al. A comparison of the Thlaspi caerulescens and Thlaspi arvense shoot transcriptomes. New Phytologist. 2006;170(2):239-260
  85. 85. Hu R et al. Physiological responses and tolerance mechanisms to Pb in two xerophils: Salsola passerina Bunge and Chenopodium album L. Journal of Hazardous Materials. 2012;205:131-138
  86. 86. Rejeb KB et al. Evaluation of the Cd2+ phytoextraction potential in the xerohalophyte Salsola kali L. and the impact of EDTA on this process. Ecological Engineering. 2013;60:309-315
  87. 87. Osman HE, Badawy RK. Effect of pollution on the chemical content and secondary metabolites of Zygophyllum coccineum and Tamarix nilotica. Egyptian Pharmaceutical Journal. 2013;12(1):73
  88. 88. De La Rosa G et al. Role of ethylenediaminetetraacetic acid on lead uptake and translocation by tumbleweed (Salsola kali L.). Environmental Toxicology and Chemistry. 2007;26(5):1033-1039
  89. 89. Lefèvre I, Corréal E, Lutts S. Cadmium tolerance and accumulation in the noxious weed Zygophyllum fabago. Botany. 2005;83(12):1655-1662
  90. 90. Carvalho KM, Martin DF. Removal of aqueous selenium by four aquatic plants. Journal of Aquatic Plant Management. 2001;39:33-36
  91. 91. Ebbs S et al. Phytoextraction of cadmium and zinc from a contaminated soil. Journal of Environmental Quality. 1997;26(5):1424-1430
  92. 92. Prasad M, Tewari JC. Prosopis juliflora (Sw) DC: Potential for bioremediation and bioeconomy. In: Bioremediation and Bioeconomy. 2016. pp. 49-76
  93. 93. Shukla O et al. Growth responses and metal accumulation capabilities of woody plants during the phytoremediation of tannery sludge. Waste Management. 2011;31(1):115-123
  94. 94. Nie M et al. Understanding plant-microbe interactions for phytoremediation of petroleum-polluted soil. PLoS One. 2011;6(3):e17961
  95. 95. Frick C, Germida J, Farrell R. Assessment of phytoremediation as an in-situ technique for cleaning oil-contaminated sites. In technical seminar on chemical spills. 1999. Environment Canada; 1998
  96. 96. Njoku K, Akinola M, Oboh B. Phytoremediation of crude oil contaminated soil: The effect of growth of Glycine max on the physico-chemistry and crude oil contents of soil. Nature and Science. 2009;7(10):79-87
  97. 97. Nedjimi B, Daoud Y. Cadmium accumulation in Atriplex halimus subsp. schweinfurthii and its influence on growth, proline, root hydraulic conductivity and nutrient uptake. Flora-Morphology, Distribution, Functional Ecology of Plants. 2009;204(4):316-324
  98. 98. Lutts S et al. Heavy metal accumulation by the halophyte species Mediterranean saltbush. Journal of Environmental Quality. 2004;33(4):1271-1279
  99. 99. Conesa H et al. Influence of soil properties on trace element availability and plant accumulation in a Mediterranean salt marsh polluted by mining wastes: Implications for phytomanagement. Science of the Total Environment. 2011;409(20):4470-4479
  100. 100. Manousaki E, Kalogerakis N. Phytoextraction of Pb and Cd by the Mediterranean saltbush (Atriplex halimus L.): Metal uptake in relation to salinity. Environmental Science and Pollution Research. 2009;16(7):844-854
  101. 101. Hegazy A, Abdel-Ghani N, El-Chaghaby G. Phytoremediation of industrial wastewater potentiality by Typha domingensis. International Journal of Environmental Science and Technology. 2011;8(3):639-648
  102. 102. Fediuc E, Erdei L. Physiological and biochemical aspects of cadmium toxicity and protective mechanisms induced in Phragmites australis and Typha latifolia. Journal of Plant Physiology. 2002;159(3):265-271
  103. 103. Paz-Alberto AM et al. Phytoextraction of lead-contaminated soil using vetivergrass (Vetiveria zizanioides L.), cogongrass (Imperata cylindrica L.) and carabaograss (Paspalum conjugatum L.). Environmental Science and Pollution Research International. 2007;14(7):498-504

Written By

Kamal Usman, Mohammad A. Al-Ghouti and Mohammed H. Abu- Dieyeh

Submitted: November 18th, 2017 Reviewed: January 12th, 2018 Published: June 27th, 2018