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Review ArticleDOI Number : 10.36811/gjcee.2019.110006Article Views : 35Article Downloads : 21

Phytoremediation of Soil Contaminated with Petroleum Hydrocarbons: A Review of Recent Literature

Kuok Ho Daniel Tang

Department of Environmental Engineering, Curtin University Malaysia, Miri, Sarawak, Malaysia

*Corresponding Author: Kuok Ho Daniel Tang, Bioprocess & Technology Research Cluster, Department of Environmental Engineering, Curtin University Malaysia, CDT250, 98009 Miri, Sarawak, Malaysia, Email: daniel.tang@curtin.edu.my 

Article Information

Aritcle Type: Review Article

Citation: Kuok Ho Daniel Tang. 2019. Phytoremediation of Soil Contaminated with Petroleum Hydrocarbons: A Review of Recent Literature. Glob J Civil Environ Eng. 1: 33-42.

Copyright: This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited. Copyright © 2019; Kuok Ho Daniel Tang

Publication history:

Received date: 29 November, 2019
Accepted date: 04 December, 2019
Published date: 06 December, 2019

Abstract

Booming anthropogenic activities is the main reason of widespread contamination of soil by petroleum hydrocarbons, resulting in environmental, health and socio-economic concerns. Remediation of contaminated soil has received much attention including phytoremediation which has the advantages of being low cost and technologically uncomplicated. Numerous papers on phytoremediation have been published and this review aims to examine selected studies on phytoremediation in the past five years to deduce the study trend and make recommendations for the way forward. The review shows an increasing number of studies combining phytoremediation with other methods particularly the physical methods such as soil amendment, electrokinetic remediation and surfactant application, as well as bioremediation using fungi and bacteria. There is increasing interest to investigate the synergy of these methods which leads to co-applications of one or more remediation methods with phytoremediation. Such co-applications often yield higher petroleum hydrocarbons removal rates in shorter time. Future studies can also include chemical remediation in the synergistic studies of phytoremediation and other remediation methods.

Keywords: Phytoremediation; Bioremediation; Crude oil; PAHs; Petroleum Hydrocarbons

Introduction

Increasing urbanization, industrialization, agriculture and transportation have resulted in widespread soil contamination, which has been made worse by a lack of regulation and law enforcement. While burgeoning anthropogenic activities cause accidental leakage and spillage of contaminants into the environment, inadequate regulation and enforcement provide loopholes for intentional disposal and discharges of contaminants which often lead to large scale pollution [1,2].

Soil contamination is generally defined as the occurrence of a substance above the normal concentration in soil, thus causing deleterious effects on non-target organisms. The contaminants are organic and inorganic in nature, each consisting of a myriad of substances. The most common organic contaminants are petroleum hydrocarbons consisting largely of the aliphatic and aromatic compounds [3,4]. Petroleum-derived non-hydrocarbons such as sulphur compounds, metallo-porphyrins and asphaltenes also constitute the organic contaminants. These contaminants are released into the environment primarily via the combustion and use of fossil fuels as well as the use of solvents, pesticides and pharmaceutical [2].

Trace elements are the main inorganic soil contaminants. Trace elements are cationic metals and oxyanions originating from rock formation and weathering, usually present as natural components of soil at concentration less than 1g kg-1 [4]. Trace elements such as zinc, copper, iron and manganese are crucial to support living processes but could raise health concerns at elevated concentrations. Other instances of trace elements like lead, mercury, arsenic and cadmium are toxic to organisms even at low concentrations [5]. Though natural processes such as volcanic activities and rock weathering contribute to high background levels of trace elements in soil, anthropogenic activities including mining, smelting, construction and agriculture aggravate inorganic soil pollution, particularly due to unnaturally high levels of lead, chromium, arsenic, zinc, cadmium, cupper and mercury in soil [4].

Soil contamination is a serious threat to soil functions especially in the Europe, Eurasia and North Africa. In the 1990s, the area of contaminated soil was estimated at 22 million hectares [6] but later regional data showed that the figure was most likely underestimated. Based on a report in 2015, the Chinese Environmental Protection Ministry estimated 16% of soil in China and 19% of its agricultural soil fell in the ‘polluted’ category [7]. In the European Economic Area and its allied West Balkan countries collectively known as EEA-39, there were about 3 million sites likely to have been polluted [8] whereas in the US, the number of polluted sites classified as Superfund National Priorities was approximated at above 1300 [9]. An approximated total of 80000 contaminated sites scattered over Australia in 2010 [10]. The extent of global soil contamination underscores the severity and extensiveness of the problem which demands attention and action.

Soil contamination is linked to environmental and health concerns which have socio-economic implications. Aromatic hydrocarbons, particularly the polycyclic aromatic hydrocarbons (PAHs) are hydrophobic and are persistent in the aquatic and terrestrial environment where they frequently form a film on water surface or adsorb to sediment particles [11]. PAHs are known to demonstrate mutagenic and carcinogenic properties [11]. Trace metals such as ionic arsenic, cadmium, mercury and lead are highly toxic and methylated mercury exhibits higher toxicity than ionic mercury [5]. Toxicity associated with these contaminants can render the affected lands unsuitable for agriculture and habitation. This affects food production which impacts food security, and concurrently impedes residential and commercial development [4]. Bioaccumulation and biomagnification of the contaminants in the food chains, as well as direct exposure to the contaminants, can cause health problems such as poisoning and illnesses [2].

Rising demand for and use of fossil fuels and petrochemicals result in more and more lands being contaminated with petroleum hydrocarbons [12]. However, due to comparatively more widespread contamination of soil by trace elements, there is higher proportion of literature dedicated to phytoremediation of trace elements or heavy metals in soil. With mounting concerns on the impacts resulted from the presence of petroleum hydrocarbons in soil, there is a need to examine studies related to phytoremediation of soil contaminated with petroleum hydrocarbons. This review therefore aims to present the recent progress made in phytoremediating soil polluted by petroleum hydrocarbons and make recommendations for the way forward.

Methods of Remediating Soil Contaminated by Petroleum Hydrocarbons

Three groups of methods are commonly used for remediation of soil contaminated by petroleum hydrocarbons, i.e. physical methods, chemical methods and biological methods [11]. Physical methods include physical sorting, soil washing and electrokinetic remediation but soil washing using solvents and surfactants are more suitable for removal of petroleum residues [13]. Electrokinetic remediation was initially intended for removal of trace elements from soil using low intensity direct current discharged into soil via an array of electrodes [14]. The electric current induces electric gradient which propels movement of contaminants via mechanisms such as electro-osmosis and diffusion [15]. Electrochemical remediation was later modified to enable removal of organic contaminants particularly the water-soluble fractions and was used with other methods such as soil flushing to treat soil contaminated with both PAHs and trace elements [15].

Chemical methods are characterized by redox reactions, photochemical degradation and thermal desorption. These methods are often better-suited for remediation of petroleum hydrocarbons compared to the physical methods [11]. The redox remediation uses oxidizing agents like hydrogen peroxide and permanganate to break down aromatic hydrocarbons while photochemical degradation is a natural process where PAHs absorb ultraviolet rays of the sun and undergo photodimerization and photooxidation in the degradation pathways [16]. Thermal desorption is more accurately a physico-chemical method using heat to degrade and volatilize contaminants from the soil without combustion. This method is appropriate for removal of gaseous trace elements and volatile organic compounds [12].

Biological methods can be further classified into bioremediation and phytoremediation. Bioremediation applies microorganisms especially bacteria and fungi to remove soil contaminants or break them down into harmless compounds via, for instance mineralization during which contaminants are used to produce carbon and energy [17]. Bioremediation is effective against 2-ring and 3-ring PAHs but has limited ability to remove more resistant contaminants which eventually form toxic metabolites in the microorganisms [18]. Phytoremediation removes contaminants from the environment by using plants and their micro-symbionts. It also facilitates contaminants removal via amendment of soil and agronomic practices [18]. A few mechanisms are involved in phytoremediation, namely phytovolatilization, phytodegradation, phytoextraction, phytostabilization, phytostimulation and rhizofiltration (Figure 1).

gjcee1006-figure1

Figure 1: Mechanisms of Phytoremediation [2,4].

Phytovolatilization is fundamentally the release of metabolites from the leaves and stems of plants into the air after the contaminants are absorbed by the roots (Figure 1). The contaminants might have been metabolized into less hazardous compounds or, in the case of the recalcitrant ones, might not have been rendered harmless. Therefore, phytovolatilization only transfers contaminants from the soil to the air [14]. Phytodegradation uses plant enzymes such as dehalogenase and nitrilase to break down organic compounds (Figure 1). Symbiotic microorganisms also play crucial role in phytodegradation [2]. Rhizofiltration facilitates adsorption or precipitation of contaminants at the root zone and is the main mechanism for remediation of contaminated water bodies (Figure 1) [19]. Phytostimulation or rhizodegradation on the other hand, utilizes microorganisms attached to the rhizosphere of plants to break down organic contaminants and they benefit from the symbiotic relationship by having access to nutrients in root exudates secreted by plants (Figure 1) [2]. Phytostabilization and phytoextraction are more relevant to remediation of trace elements, via immobilizing the elements in the root zone in the former, as well as extracting and hyperaccumulating the elements in the latter [4].

Phytoremediation of Petroleum Hydrocarbons

Many plant species have been identified to possess the ability in remediating soil contaminated with petroleum hydrocarbons and phytoremediation has been subject to extensive studies over the years. Due to the number of studies conducted in this area, this review focuses on the studies conducted in the past 5 years starting from the most recent ones as shown in Table 1 below and does not attempt to cover all studies published in the period.

Table 1: Summary of Selected Phytoremediation Studies Conducted between 2014 and 2019.

Source

Soil contaminant

Plant

Method

Parameter and Removal Rate

Duration

Zhen et al., 2019 [20]

Petroleum

Spartina anglica

Spartina anglica cultivation with and without biochar, rhamnolipid and rhamnolipid-modified biochar

Total petroleum hydrocarbons (TPHs):

Planted soil (19.1%); planted soil with biochar (27.7%); planted soil with biochar and rhamnolipid (32.4%); planted soil with rhamnolipid-modified biochar (35.1%)

60 days

Baoune et al., 2019 [21]

Crude petroleum; pure PAHs (phenanthrene, pyrene and anthracene)

Zea mays

Zea mays seedlings inoculated with Streptomyces sp. Hlh1.

Petroleum crude hydrocarbons (70%); phenanthrene (61%); pyrene (59%) and anthracene (46%)

14 days

Iqbal et al., 2019 [22]

Diesel

Lolium perenne; Arabidopsis thaliana

Plant-microbe phytoremediation system by inoculating the plants with Pseudomonas sp. (J10) (KY608252)

TPHs:

L. perenne (small variant) system (45.6%); L. perenne (jumbo variant) system (24.5%); A. thaliana system (6.2%)

 

20 days

Tang & Angela, 2019 [12]

Crude oil

Pteris vittata; Epipremnum aureum; Mucuna bracteata; Imperata cylindrica

Screening study with plants commonly encountered in Malaysia at 5% crude oil contamination by weight

TPHs:

Epipremnum aureum (50.4%); Imperata cylindrica (39.5%); Pteris vittata (36%); Mucuna bracteata (30.9%)

42 days

Tang & Law, 2019 [7]

Crude oil

Mucuna bracteata

Mucuna bracteata with and without application of fertilizer

TPHs:

5% contamination with fertilizer (36.8%) and without fertilizer (26.5%); 10% contamination with fertilizer (27.5%) and without fertilizer (26%); 15% contamination with fertilizer (32.4%) and without fertilizer (22.5%)

63 days

Rocha et al., 2019 [23]

Petroleum

Helianthus Annuus

Phytoremediation (PR), electrokinetic remediation (ER) –Reverse Polarity (RP), ER-direct current (DR), ER-PR-DR, ER-PR-RP

TPHs:

PR (16%); ER-RP (68%); ER-DC (57%); ER-PR-DC (76%); ER-PR-RP (84%)

20 days

Huang et al., 2019 [24]

Diesel

Alternanthera philoxeroides

Phytoremediation with and without adding Se (0.5 or 1.5 mg/kg)

Soil diesel concentration:

Without Se (20.1±0.55%); with Se (35.2±3.6%)

60 days

Hussain et al., 2018 [25]

Crude oil

Italian ryegrass (Lolium multiflorum)

Italian ryegrass (IR) cultivated with and without a combination of biochar (BC), compost (CM) and microbial consortia (MC)

TPHs:

IR with no amendment (47%); IR+BC (65%); IR+CM (70%); IR+MC (73%); IR+BC+CM (75%); IR+BC+MC (82%); IR+CM+MC (84%); IR+BC+MC+CM (85%)

75 days

Asemoloye et al., 2017 [26]

Crude oil

Megathyrsus maximus

Megathyrsus maximus planted in soil contaminated with 10%, 20%, 30% and 40% crude oil, in the presence of cultures of four new rhizospheric fungi mixed with spent mushroom compost (SMC)

Total polyaromatic hydrocarbons (TPAHs):

Soil+plant (44.3%); soil+fungi-SMC mixture (32.6%); 0.5kg fungi-SMC mixture+plant+soil with 10% crude oil (69.7%); 1kg fungi-SMC mixture+plant+soil with 20% crude oil (83.0%); 1.5kg fungi-SMC mixture+plant+soil with 30% crude oil (95.3%); 2.5kg fungi-SMC mixture+plant+soil with 40% crude oil (89.6%)

90 days

Liao et al., 2016 [13]

Crude oil

Zea mays

Phytoremediation facilitated by two biosurfactants (rhamnolipid and soybean lecithin) and a synthetic surfactant (Tween 80)

TPHs:

Soybean lecithin (62%); rhamnolipid (58%); Tween 80 (52%)

3 months

Kösesakal et al., 2016 [27]

Crude oil

Azolla filiculoides

Azolla filiculoides cultivated in nitrogen-free Hoagland nutrient solution spiked with increasing crude oil from 0.005% to 0.5% by volume

Azolla filiculoides tolerant to 0.1% to 0.2% of crude oil.

 

0.05 – 0.2% oil contamination:

Total aliphatic (94-73%); phenanthrene (81-77%)

 

0.3 – 0.5% oil contamination: Total aliphatic (71-63%); phenanthrene (75-71%)

15 days

Hou et al., 2015 [28]

Petroleum

Testuca arundinacea

Fertilized and unfertilized soil with and without Testuca arundinacea (TA) as well as with and without inoculation with plant growth promoting bacteria

Aliphatic hydrocarbons:

Control – no fertilizer (28.5%); fertilizer (F) (43.1%); F+TA (52.9%); F+TA+ Klebsiella sp. (D5A) (62.6%); F+TA+ Pseudomonas sp. (SB) (67.9%)

PAHs:

Control (34.7%); F (38.7%); F+TA (49.6%); F+TA+D5A (58.1%); F+TA+SB (62.9%)

4 months

Moubasher et al., 2015 [29]

Crude oil

Bassia scoparia

Natural and sterilized soil with and without Bassia scoparia, watered and not watered with Hoagland nutrition solution

TPHs:

Watered natural soil + plant (57.7±1.29%); watered sterilized soil + plant (51.1±1.53%); watered natural soil (46.3±2.31%); watered sterilized soil (22.0±0.54%); unwatered natural soil (9.2±0.52%); unwatered sterilized soil (3.2±0.13%)

5 months

Ribeiro et al., 2014 [30]

Crude oil

Juncus maritimus; Phragmites australis

Natural attenuation,

Biostimulation and bioaugmentation in colonized salt marsh sediments

TPHs:

Natural attenuation: J. maritimus (12%); P. australis (16%).

Biostimulation: J. maritimus (2.1%); P. australis (11%).

Bioaugmentation: J. maritimus (4.4%); P. australis (11%)

150 days

Bramley-Alves et al., 2014 [31]

Special Antarctic Blend (SAB)

Subantarctic native tussock grass (Poa foliosa)

Seedlings cultivated in soil polluted with 1000, 5000 and 10000 mg/kg SAB

TPHs:

1000 mg SAB/kg soil (41%); 5000 mg SAB/kg soil (45%); 10000mg SAB/kg soil (48%)

2 months

Table 1 shows an increasing trend of studies on the synergistic effects of phytoremediation with other remediation methods such as bioremediation, surfactants and electrokinetic remediation though conventional phytoremediation studies with and without addition of fertilizer have also been conducted [13,21,23]. Phytoremediation studies have conventionally been associated with biostimulation via addition of fertilizers [7]. but have lately been increasingly linked to bioaugmentation with bacteria or fungi [26,28]. There is also interest to examine the effect Se in increasing the efficiency of phytoremediating plant [24]. The common plants used for phytoremediation studies are Zea mays, Helianthus Annuus, Sorghum bicolor, and Lolium multiflorum though the list of plants with phytoremediating ability is growing with new additions from screening studies. Examples of the new additions are Azolla filicuilodes, Mucuna bracteata and Epipremnum aureum.

The duration of phytoremediation studies in Table 1 ranges from 14 days to 5 months and the hydrocarbon removal rates do not correspond with the duration of study. In fact, the methods and plants used have greater influence on hydrocarbon removal. For instance, in 14 days, Baoune et al. reported removal of up to 70% of petroleum crude hydrocarbons and 61% of phenanthrene from soil [21]. Kösesakal et al., however, reported up to 94% total aliphatic removal from liquid medium contaminated with 0.05-0.2% crude oil and the removal rates decreased with increasing levels of contamination [27]. In the case of soil contamination, higher removal rates are often achieved when phytoremediation is used with bioaugmentation particularly with selected petroleum degrading fungi and bacteria, as well as electrokinetic remediation.

Conclusion

This review demonstrates that current phytoremediation studies are moving in the direction of examining the synergy between phytoremediation and other remediation methods. This review also underscores the potential discovery of new plants with ability to phytoremediate soil contaminated with petroleum hydrocarbons. It recommends that future studies can continue to look into applying phytoremediation with other remediation methods particularly electrokinetic method. Further studies can also explore the potential synergy between phytoremediation and chemical remediation which has not received as much attention as the association of phytoremediation with physical remediation and bioremediation.

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