Microbial surfactants in environmental technologies Текст научной статьи по специальности «Сельское хозяйство, лесное хозяйство, рыбное хозяйство»

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UDC 759.873.088.5:661.185

doi: 10.15407/biotech8.04.021

MICROBIAL SURFACTANTS IN ENVIRONMENTAL TECHNOLOGIES

T. P. PIROG, A. D. KONON, I. V. SAVENKO

National University of Food Technologies, Kyiv, Ukraine

E-mail: [email protected]

Received 10.03.2015

It was shown literature and own experimental data concerning the use of microbial surface active glycolipids (rhamno-, sophoro- and trehalose lipids) and lipopeptides for water and soil purification from oil and other hydrocarbons, removing toxic heavy metals (Cu2+, Cd2+, Ni2+, Pb2+), degradation of complex pollution (oil and other hydrocarbons with heavy metals), and the role of microbial surfactants in phytoremediation processes.

The factors that limit the use of microbial surfactants in environmental technologies are discussed. Thus, at certain concentrations biosurfactant can exhibit antimicrobial properties and inhibit microorganisms destructing xenobiotics. Microbial biodegradability of surfactants may also reduce the effectiveness of bioremediation. Development of effective technologies using microbial surfactants should include the following steps: monitoring of contaminated sites to determine the nature of pollution and analysis of the autochthonous microbiota; determining the mode of surfactant introduction (exogenous addition of stimulation of surfactant synthesis by autochthonous microbiota); establishing an optimal concentration of surfactant to prevent exhibition of antimicrobial properties and rapid biodegradation; research both in laboratory and field conditions.

Key words: microbial surfactants, bioremediation.

Surfactants are widely used in different fields of industry that is why the demand for their synthetic analogues is continually increases. At the same time the modern development of biotechnology and growing attention to environment defense are the source of interest to microbial surfactants as an alternative way of chemical analogues. Due to environmental safety, the ability to emulsify hydrophobic compounds and increase the efficiency of microbial decomposition of xenobiotic, surfactants are promising for use in environmental technologies.

Over the past decades, the environment has got a huge amount of industrial waste, agricultural chemicals and products of their partial transformations that are unique or rare in nature. This resulted in a negative impact on all levels of organization of living matter and that balance breaks the balance that was created over millions of years, so that there is a real threat to the sustainable functioning of ecosystems.

Today oil is the main source of energy worldwide, while the probability of getting it into the environment, leading to negative

consequences [1]. Since 1992 the world has held more than 20 oil spills [http:/www.endgame. org/oilspills.htm], which led to economic losses and violations of ecological balance. To eliminate the consequences of such accidents physical and mechanical methods are usually used, but they are not always effective enough. According to the Office of Technology Assessment (Office of Technology Assessment, USA) after large-scale disaster, it is possible to remove only 10-15% of oil by mechanical methods [1].

To eliminate oil spill there are some promising biological methods, based on direct introduction of petrooxidizing microorganisms (bioaugmentation) or using various substances that stimulate the natural (autochthonous) microbiota (biostimulation) such as microbial surfactants [2, 3]. For the first time the possibility of using microorganisms for the biodegradation of oil in marine sediments was described by Jones et al. 1983 [4]. In the future, scientists expanded the knowledge of oil destructors and conditions of their application [5-8].

Recently, interest in microbial surfactants is increasing [9-14], due to significant progress

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in the development of technologies for their cheaper production [15, 16] and the rapid trend development to protect the environment [17].

Due to environmental safety, the ability to emulsify hydrophobic compounds, form complexes with heavy metals and improve the effectiveness of some xenobiotics microbial degradation of surfactant may acquire wide application in environmental technologies [1824]. In addition, these metabolites are unique because they can be obtained from industrial waste and then be used for destruction of pollutants, i.e. during the production and application of microbial surfactants, there is an effect of “double” environment cleaning [25, 26].

The mechanisms of oil destruction

The literature describes several mechanisms of oil degradation under surfactants, one of which is associated with desorption, mobilization or solubilization of organic pollutants that leads to increasing their bioavailability to microorganisms, and another is related with increased cell surface hydrophobicity of most destructors [27, 28]. According to the first mechanism, the removal of hydrophobic xenobiotics from the soil can occur in two ways, depending on the concentration of surfactant. For concentrations of surfactants, lower the critical micelle concentration (CMC), there is the phenomenon of mobilization, resulting in reduced capillary and interfacial forces that hold the oil in the soil, and it is observed the increase of contact angle of the surfactant with the system oil/soil [19]. If the concentration of surfactant is at CMC level and above, the process of solubilization takes place. In this case, oil is placed in micelles, which hydrophobic ends are placed inside and hydrophilic — outside. It provides solubility of hydrophobic contaminant [29, 30]. It was carried out the electron microscopy study of the absorption of n-alkanes by Pseudomonas aeruginosa and it was found that by its nature the phenomenon is similar to pinocytosis [31].

There is another mechanism, which was described in [32]. It was noted the chemical and structural changes of surface structures of P. aeruginosa in case of introduction of the rhamnolipids and hexadecane. It was shown that in the presence of surfactants in very low concentrations it is observed the release of cell wall lipopolysaccharide from pseudomonas cell wall, which leads to an increase in surface hydrophobicity. There are reports [33] that rhamnolipids do not affect the cell

wall lipopolysaccharide, but can change the composition of the outer membrane proteins.

Mohanty et al. [34] compared the mechanisms of naphthalene adsorption by Burkholderia multivorans (NG1) in the presence of Triton X-100 and JBR-515 rhamnolipids. Synthetic surfactants increased naphthalene bioavailability due to its emulsification and maintaining interphase contact with the cell while microbial surfactants solubilized the organic pollutant.

Water and soil purification from oil and other hydrocarbons

It was offered a variety of options using microbial surfactants for cleaning: using of their microorganisms-producers to utilize oil and oil products; treating the most contaminated sites with surfactant solutions in bioreactors; treating contaminated areas with these solutions to solubilize hydrocarbons. The last one stimulates the development of natural petrooxidizing microbiota [35]. It was demonstrated the ability of Pseudomonas sp. LP1 to metabolize oil and diesel fuel [36], the degree of destruction was 92.34% and 95.29% respectively. There are reports [37] about the ability of Brevibacterium sp. PDM-3 to degrade phenanthrene and other polyaromatic hydrocarbons (93.92%). It was noted high rates of degradation of oil, aliphatic and aromatic hydrocarbons (85-97%) in case of introduction of sophorolipids [38]. Das et al. [39] showed the effectiveness of the introduction of Bacillus subtilis DM-04, P. aeruginosa M and P. aeruginosa NM in oil contaminated soil: on the 120th day the general level of petroleum hydrocarbons fell from 84 to 21-39 g/kg soil, while in the control variant (without introduction of microorganisms), the figure was 83 g/kg. Fan et al. [40] found that in case of introduction of Candida tropicalis SK21, that able to synthesize surfactants in soil contaminated by oil (16.3 g/kg), on the 180th day 83% of hydrocarbons were degraded, while without yeast introduction this figure was only 61%. It was described the ability to use cells of Pseudomonas cepacia CCT6659, glycolip-ids synthesized by this strain and surfactant mixtures with the cell producer for bioremediation of soils from oil [41]. Oil degradation by 83% was observed after 10 days of common use of glycolipids and cells of P. cepacia CCT6659. It was shown the use of Acinetobacter sp. D3-2, which synthesizes lipopeptides, for oil destruction (82%) at 30 °C in the presence of 3% NaCl [42]. Indian scientists [43] purified and identified the strain Planomicrobium chinense B6,

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which is capable of degradation of diesel fuel containing linear C14-C36 n-alkanes, thanks the synthesis of emulsifier. Resistance of B6 strain to high temperatures, toxic metals and moderate salt concentration makes it promising for use in bioremediation processes of soils in a tropical climate. Diab et al. [44] established the possibility of using the supernatant P. aeruginosa SH 29 containing surfactant (index emulsification is 62%) for the cleaning of oil tanks. In subsequent studies, the authors showed that after treatment the soil with the supernatant of surfactant producers Bacillus spp. SH 20 and SH 26 (10 ml/100 g) the degree of degradation of oil sludge was 34 and 28% respectively.

In another study [45] authors showed that the use of culture fluid and corresponding supernatant of P. aeruginosa RS29, containing monorhamnolipids removed respectively 85 and 55% of hydrocarbons from the sludge.

It was described the theoretical possibility about using of surfactants (10 mg/ml) from probiotic strain Lactococcus lactis in the process of remediation of oil-contaminated water (10 ml/40 ml) [46]. Recently, it has been reported about the isolation and identification of Rhodococcus sp. JZX-01 that is capable of surfactant synthesis and degradation of oil in water (65.27% in 9 days), even at low temperatures and high salinity [47]. In addition, this strain is able to utilize long-chain hydrocarbons (C31-C38) and branched alkanes. Jain et al. [48] reported about the potential use of alkaliphilic bacteria Klebsiella sp. RJ-03 in the process of remediation due to their ability to synthesize surfactants from cheap raw materials (corn flour) and their stability over a wide range of pH and temperature. It was shown the possibility of using Serratia marcesencs L-11 for the degradation of polyaromatic hydrocarbons due to the strain ability to synthesize surfactants and catechol-1,2-dehydrogenase [49].

It was found that the use of synthetic dodecyl sulfate and rhamnolipids resulted in the removal of oil from the soil by 44-46%, whereas saponin (surfactants of vegetable origin) provided around 27% [50]. In case of introduction of 10 g/l sophorolipids to the soil contaminated by 2-methylnaphtalene it was removed 30% of xenobiotics [38].

There are some data that efficiency of microbial surfactants is not inferior, and in some cases superior compared with synthetic Span 20/80/85. Lai et al. [19] compared the efficiency of rhamnolipids and the microbial surfactant with synthetic surfactants Tween

80 and Triton X-100 for cleaning the soil from oil (oil concentration 9.3 g/kg).

The maximum degree of oil degradation (62-63%) was observed in case of the treatment with microbial surfactants, while using synthetic surfactants provide only 35-40%. It was determined the degree of soil laundering from the diesel fuel by lipopeptides from B. subtilis SPB1 and their synthetic analogues — SDS and Tween 80 [51].

It was established that microbial surfactants not inferior to the efficiency of synthetic analogues and thanks their use it was removed up to 87% of fuel for 24 hours at 30 °C. In another study [12] the authors showed that using glycolipids from Candida sphaerica UCP0995 it was possible to get the degree of laundering sand from motor oil equal 95%. That makes the use of surfactants of this strain perspective in the process of bioremediation.

Complex technology of cleaning soil from oil was described in articles of Kildisas et al. [52] and Baskys et al. [53]. This technology consisted of several stages: laundering soil from oil using surfactants, destruction of residual oil by bioaugmentation and phytoremediation. As a result, at the pilot plant area of 340 m2 which contained 1,000 m3 of soil, the concentration of oil was reduced from 180-270 to 3.2-7.3 g/kg.

Moldes et al. [54] investigated the possibility of using surfactants from Lactobacillus pentosus CECT-4023 T (ATCC-8041) in the remediation of soil from octane. It was shown that introduction of surfactants led to activation of natural soil microbiota and after 15 days, it was observed destruction of 59 octane and 63% of its initial concentration by 700 and 70 000 mg/kg, respectively. In control variant (without the addition of surfactants), it was degraded 1 and 24% of octane respectively. In subsequent studies, this group of scientists compared the effectiveness of the use of surfactants from L. pentosus CECT-4023 T (ATCC-8041) and dodecyl sulfate for the purification of soil from octane (7,000 mg/ kg) [55]. It was found that in case of using microbial surfactants (2.65 mg/l) for 15 days the degree of octane degradation was 65.1%, while the presence of synthetic surfactants — only 37.2%.

Introduction of rhamnolipids, sophoro-lipids and trehalosolipids led to the increase of efficiency for 30-50% and accelerated the soil purification from halogen derivatives for 8 days compared with the data obtained with surfactants [56]. With the addition of rhamnolipids from P. aeruginosa SP4 at

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a concentration of 250 mg/l, the degree of pyrene decomposition in soil (500 mg/kg) was 84.6%, while in the absence of surfactants — 59.8% [57].

Scientists from Latvia [58] suggested using mathematical methods of planning the experiment to predict the efficiency of microbial surfactants for cleaning the environment. The object of the study were surfactants of glycolipid nature with the commercial name AURA-PURE ST (manufacturer AURAVIA LATVIA SIA, Latvia).

It was taken into account such factors as temperature, contact time of surfactants, the concentration of surfactants in the solution. It was established that at the critical value of all conditions (35 °C, 15 min, 0.3%, mass fraction) up to 99.32% of the oil was removed.

It was shown the possibility of using untreated surfactants and solutions of treated surfactants (0.8 and 0.16 g/l) from C. sphaerica UCP 0995 for the destruction of diesel oil in different types of soil [59]. In addition, the authors studied the laundering properties of studied metabolites. It was shown that by introducing 200 ml of preparation, the degree of oil decomposition was 75, 92 and 50% in clay, muddy and sandy soil respectively (100 g/kg soil). Preparations surfactants possessed effective laundering properties: at the concentration of 0.16 g/l, they removed 88% of the engine oil from the soil. Treatment with untreated surfactants of the cotton fabric tissue contaminated with oil (3 g of oil for 25 m2 of fabric tissue), resulted in removal of 41% removal of hydrocarbons.

Cerqueira et al. [60] studied the ability of 45 isolates to use oil sludge as the sole source of carbon and energy. Basing on the analysis of 16S rRNA among the studied bacteria, it was selected and identified five strains (Stenotrophomonas acidaminiphila BB5, Bacillus megaterium BB6, Bacillus cibi, P. aeruginosa and Bacillus cereus BS20), which can be promising for use in environmental technology for its ability to synthesize surfactants and resistance to high concentrations of oil sludge (up to 30%).

The rapid development of biodiesel involves the search for effective methods of cleaning the environment under conditions of accidents. Authors [61] studied the mixture of diesel and biodiesel (B20), that it received from areas contaminated by hydrocarbons/ethers and consortium of microorganisms that was able to the decomposition of pollutants. According

to the results of enzymatic analysis and capacity of surfactant synthesis, it was elected four bacterial isolates — B. megaterium,

B. pumilus, P. aeruginosa and Stenotrophomonas maltophilia, which are planned to use for cleaning the polluted environment. In other studies [62], rhamnolipid adding under aeration conditions increased effectiveness of decomposition B20. However, it made no influence on the rate of destruction of diesel fuel obtained from oil.

Our research has shown that the presence of surfactant preparations from Acinetobacter calcoaceticus IMB В-7241, Rhodococcus erythropolis IMB Ac-5017 and Nocardia vaccinii IMB В-7405 as cultural liquid and a supernatant resulted in the degree of oil degradation in the water 80-94% (Table 1), and in the soil — 67-86% (Table 2).

Generalizing data on the degradation of xenobiotic surfactants are given in Table 3.

Removal of toxic metals

It is known that heavy metals are not biodegradable, but the bacteria can change their mobility and toxicity due to chemical reactions (oxidation-reduction reactions, alkylation, etc.), the formation of complexes with synthesized metabolites or intracellular accumulation [78]. To extract metals ex situ, contaminated soil is collected in glass tubes and washed with surfactants (it is called “soil washing”). To do it in situ — create drainage pipe and trench, which are used for injection and pumping of surfactants (“soil flushing”) [79, 80]. There are technologies that help to separate complexes of heavy metals and surfactants by centrifugation followed by the removal of these metals [80].

The principle of removing metals from soil is based on the fact that affinity of microbial anionic surfactants to metals is stronger than metal connection with soil, so complex “surfactant-metal” is easily washed away. Removal of metals from soil with cationic surfactants is based on the principle of ion exchange [27, 79, 81, 82]. Scheme of extracting metals from the soil using surfactants is shown in Fig 1.

Juwarkar et al. [84] showed that 0.1% dirhamnolipids from P. aeruginosa BS2 effectively removed metals from the soil in the following sequence Cd2+ = Cr2+ > Pb2+ = Cu2+ > Ni2+. In addition, anionic surfactants synthesized by marine organisms were effective in soil remediation to remove Pb2+ and Cd2+ [85].

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Table 1. Indicators of water purification from oil using surfactant preparations from A. calcoaceticus ІМВ В-7241, R. erythropolis ІМВ Ac-5017 and N. vaccinii ІМВ В-7405

Strain-producer of surfactants Surfactant preparation Concentration of surfactant preparation,% Concentration of remaining oil, g/l The degree of oil destruction *,%

А. calcoaceticus ІМВ В-7241 Cultural liquid 5 0.20 ± 0.010 92.3

10 0.32 ± 0.015 87.7

15 0.36 ± 0.018 88.2

Supernatant 5 0.44 ± 0.022 83.1

10 0.32 ± 0.015 85.7

15 0.38 ± 0.019 85.4

R. erythropolis ІМВ Ac-5017 Cultural liquid 5 0.18 ± 0.009 93.1

10 0.17 ± 0.008 93.5

15 0.17 ± 0.008 93.5

Supernatant 5 0.42 ± 0.021 83.9

10 0.40 ± 0.020 84.6

15 0.39 ± 0.020 85.0

N. vaccinii ІМВ В-7405 Cultural liquid 5 0.15 ± 0.007 94.2

10 0.29 ± 0.014 88.8

15 0.40 ± 0.020 84.6

Supernatant 5 0.45 ± 0.022 82.8

10 0.54 ± 0.027 79.0

15 0.55 ± 0.027 79.5

Note. In calculating the degree of oil degradation, the error does not exceed 5%. Time of exposure is 30 days. Initial concentration of oil in the water is 2.6 g/l. The degree of oil degradation in control (not treated with the surfactants) is 3.5%. Here and after all meanings* — Р < 0.05 vs. control.

Table 2. The influence of cultural liquid of A. calcoaceticus !МВ В-7241, R. erythropolis ГМВ Ас-5017 and N. vaccinii !МВ В-7405 on the efficiency of soil purification from oil

Surfactant producer Concentration of cultural liquid, ml/kg of soil Concentration of remaining oil, g/kg The degree of oil destruction *,%

A. calcoaceticus ШВ В-7241 100 4.1 ± 0.21 80.8

200 3.9 ± 0.19 81.8

300 3.8 ± 0.19 82.2

R. erythropolis ШВ Ас-5017 100 7.0 ± 0.35 67.3

200 5.7 ± 0.28 73.4

300 2.9 ± 0.14 86.4

N. vaccinii ШВ В-7405 100 6.2 ± 0.31 71.0

200 5.6 ± 0.28 74.0

300 3.5 ± 0.17 83.5

Note. Initial concentration of oil in the soil is 21.4 g/kg. The degree of oil degradation in control (not treated with the surfactants) is 5.8%.

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Table 3. Using microbial surfactants in bioremediation

Type of surfactant Contaminant Initial concentration of contaminant, g/l Destructor Efficiency of destruction, % Destruction period, days Refe- rences

1 2 3 4 5 6 7

Rhamnolipids Phenantrhrene 10 Monoculture of Sphingomonas sp. 99 10 [63]

Rhamnolipids Anthracene 0.025 Monoculture of Sphingomonas sp. and Pseudomonas sp. 52 18 [64]

Monorhamno- lipids Hexadecane 0.5 Monoculture of C. tropicalis 93 4 [65]

Rhamnolipids, emulsan, surfactants of native microbiota Pyrene 0.05 Monoculture of P. fluorescens 98 10 [66]

Rhamnolipids Polycyclic aromatic hydrocarbons 12.85 g/kg of soil Alfalfa, arbuscular mycorrhiza consortium 61 90 [67]

Monorhamno- lipids Phenol 0.5 Monoculture of C. tropicalis 99 30 hours [68]

Rhamnolipids Petroleum hydrocarbons 0.823 Autochthonous marine microbiota, biogenic elements 59 5 [69]

Rhamnolipids Petroleum hydrocarbons (C19-C34 alkanes) 5 Autochthonous marine microbiota 96 18 [70]

Rhamnolipids Phenantrhrene 500 mg/kg of soil Monoculture of Pseudomonas putida ATCC 17484 91 10 [71]

Rhamnolipids Phenantrhrene 200 mg/kg of soil Monoculture of Sphingomonas sp. 47 70 [72]

Rhamnolipids Mixture of diesel and biodiesel 15 Consortium 77 7 [73, 74]

Sophorolipids Mixture of hydrocarbons 6 mg/g of soil Autochthonous soil microbiota 97 6 [38]

Not identified Oil sludge - Mixture of bacterial cultures 91% (linear hydrocarbons) and 52% (aromatic hydrocarbons) 40 [75]

Not identified Hydrocarbons of diesel lubricants 450 mg/l Autochthonous soil microbiota 77 15 [76]

Not identified Pyrene - Monoculture of B. subtilis and P. aeruginosa 32-48 4 [77]

Note: «—» — data not shown.

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Fig. 1. Mechanism of metal purification from soil using surfactants [83]

Liu et al. [86] found that soil washing with dirhamnolipids (0.02 M) accompanied by the removal of 15.35% Cu2+ and 14.42% Pb2+. With the presence of saponins (3 g/l) and biodegradable S, S-ethylenediamine acid (10 mM) it was possible to remove 99.8% Pb2+, 85.7% Cu2+ and 45.7% PCBs [87].

The efficiency of extracting metals from contaminated soil essentially depends on further introduced substances. Thus, the number of copper and nickel cations, which were removed by rhamnolipids, was significantly increased in the presence of 1% NaOH [88]. It is believed that the addition of alkali results in dissolution of the organic fractions, which contain metals in bound form. As a result, cations become more available.

Wang and Mulligan [89] compared the efficiency of surfactants as foam and supernatant (traditional method) to remove Cd2+ and Ni2+ from the soil. The authors found that the use of surfactants as foam allows to remove 73.2% and 68.1% of Cd2+ and Ni2+ respectively, while the traditional way — only 61.7% and 51%. Similar results were described in [90]; it was shown the possibility of using saponins from soapberry and surfactant from B. subtilis (BBK006) as a foam to remove copper (6511 mg/kg), lead (4955 mg/kg) and zinc (15,090 mg/ kg) from the soil. It was established that due to surfactant addition, the degree of removal of Pb2+, Cu2+ and Zn2+ from soil after 48 hours was 1-2, 16-17 and 2124% respectively. After saponin treatment (0.15 g/l), it was removed from the soil 98% Pb2+, 95% Cu2+ and 56% Zn2+ at pH 4 and 30 °С for 72 hours.

Sorption of metals from soil greatly depends on its chemical composition. It is known that one of the components of sand soil is quartz, so in [90, 91] it was selected for the research. It was established that the use of 25 mM of rhamnolipids removed up to 91.6% of Cd2+ and 87.2% of Zn2+ from the quartz.

It was compared the efficiency of using sulfur bacteria Acidithiobacillus sp. and their mixture with the surfactant (producers: B. subtilis PCM 2021 and B. cereus PCM 2019) for the extraction of zinc (initial concentration in the mineral was 12471.4 mg/kg), copper (41237.3 mg/kg), lead (14129.9 mg/kg), nickel (13244.7 mg/kg) cadmium (1.9 mg/kg) and chromium (72.4 mg/kg) [92]. Using the second modified method (a mixture of bacteria and surfactants) was 2 times more effective at leaching chromium (23%). The degree of removal of zinc and cadmium was the same as in case of sulfur bacteria, and their mixture with surfactant, and was 48 and 93% respectively. Maximum figures of extraction of nickel and copper (48.5 and 53% respectively) were observed for the traditional method of using only bacteria.

The destruction of complex pollutants

It is known that the presence of heavy metals can decrease of effectiveness of oil degradation. That is why an important task is to find methods of environmental purification from such complex contaminants [93]. One way to reduce the toxic effects of metals on cell-destructors is their binding to calcium carbonate, phosphates, chelating agents, clay minerals, and surfactants [94-97].

Thus, it was described the possibility of using rhamnolipids, which bind metal in the complex and facilitate its removal using Burkholderia sp. through the release of lipopolysaccharide [98]. It was observed improved phenanthrene degradation by P. aeruginosa in the presence of cadmium cations with addition of rhamnolipids [99].

Singh et al. [100] showed that during the washing of soil contaminated with oil by the mixture of surfactant and phengicin from B. subtilis A21 it was possible to remove hydrocarbon 64.5% and 44.2% cadmium, cobalt 35.4%, 40.3% lead, 32.2% nickel, 26.2% copper and 32.07% zinc. Mechanisms of resistance to toxic metals, factors that affect the bioavailability of metals and

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methods of determining the impact of metals on bioremediation processes of complex pollution as well as the methods of cleaning were thoroughly described in [93].

In addition to metal, the complex contamination may contain other compounds that are toxic to microorganisms-destructors [100]. Thus, Chrzanowski et al. [101] used rhamnolipids linking homologues of chlorophenols in micelles. It reduced the toxicity towards destructor P. putida DOT-T1E. Subsequently, the authors applied this technique to improve the cleaning of wastewater polluted with oil and chlorophenol by consortium of microorganisms [102]. Nievas et al. [103] investigated bilge water — complex waste like oil fuel, composed of n-alkanes and insoluble branched, cyclic and aromatic hydrocarbons. Introduction of consortium, which synthesizes an emulsifier, provided the degree of decomposition of waste equal 58-85%, depending on their nature and accessibility for destructors.

Our data indicate that the degradation of oil in water containing various concentrations of copper cations, by surfactants from A. calcoaceticus IMB В-7241, R. erythropolis IMB Ac-5017 and N. vaccinii IMB B-7405 are significantly higher than for variants only with Cu2+ (Table 4).

The next step examined the possibility of using the surfactant from the strain IMB B-7405 in a cultural liquid to clean the water containing oil and cations of several toxic metals (Table 5). It was established that the lowest efficiency degradation of oil (65%) was observed in the presence of cadmium and lead cations in oil-contaminated water. In the presence of copper cations in the mixture, the degree of oil decomposition in water was increased. We assume that one of the mechanisms that cause the increase of oil degradation in the presence of low concentrations of copper cations may be Cu2+ stimulation of alkan hydrolase activity (initial enzymes of hydrocarbon catabolism) of both: strain-producers of surfactant and natural oil-oxidizing microbiota.

Another mechanism underlying high efficiency of oil degradation by surfactant preparations from N. vaccinii IMB B-7405 in the presence of metal cations may be the presence of protective functions in surfactants. Our experiments have shown that the removal of surfactants accompanied by death of all cells of N. vaccinii IMB B-7405 in the presence of Cu2+, Cd2+ and Pb2+ (0.05-0.5 mM), whereas in the surfactant presence under similar conditions up to 60-70% of cells were alive.

Table 4. Influence of copper cations on the oil destruction in water with the presence of cultural liquid of A. calcoaceticus ІМВ В-7241,

R. erythropolis ІМВ Ac-5017 and N. vaccinii ІМВ В-7405

Cu2+ concentration in water, mi Oil destruction * (%) after treatment with surfactants from the strain

ІМВ B-7241 ІМВ Ac-5017 ІМВ B-7405

0 75.7 73.7 74.0

0.01 98.2 95.3 98.6

0.05 98.0 80.5 98.4

0.1 95.4 N.d. 98.4

0.5 90.8 N.d. 89.0

1.0 87.6 N.d. N.d.

Note. Period of exposure is 20 days. Initial concentration of oil in water — 3.0 g/l. The degree of oil destruction in the water that is non-treated with surfactants and copper cations (control) — 2.5%. N.d. — not determined.

Table 5. Influence of cultural liquid of N. vaccinii ІМВ В-7405 (10%, volume fraction) on the oil destruction (6.0 g/l) in water in the presence of Cu , Cd2+ and Pb2+

Concentration of cations in water, mM Oil destruc- tion*,% The number of cells*, CFU/ml

Cu2+ Cd2+ Pb2+

0 0 0 76 (4.9 ± 0.24)-105

0 0.5 0.5 65 (2.1 ± 0.10)105

0.5 0 0.5 78 (6.5 ± 0.32)105

0.5 0.5 0 81 (7.1 ± 0.35)-105

0.5 0.5 0.5 82 (7.2 ± 0.36)105

Note. The number of cells in the original water (before introduction of oil, surfactants and metal cations, — control) was (2.4 ± 0.12)-103 CFU/ml. The degree of oil destruction in the water untreated with surfactants and metal cations (control) — 2.0%.

Period of exposure — 25 days.

In calculating the degree of oil degradation, the error does not exceed 5%.

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Phytoremediation

Many current reviews generalized data on the use of phytoremediation to clean the environment [104-107]. It is believed that the interaction of “plant-microorganism” significantly affects the biotransformation of organic substances. As for microbial surfactants, the effectiveness of phytoremediation can be increased by adding surfactant-synthesizing microorganisms resistant to heavy metals. Thus, it was studied the effect of cadmium-resistant Bacillus sp. J119 on the purification of contaminated soil using canola, corn, Sudan grass and tomatoes [108]. It was established that the studied strain colonized roots of all plants, but increased synthesis of biomass and uptake of cadmium was observed only for tomato. The authors concluded that the efficiency of phytoremediation depends on the type of plant and microorganism. Details of particular use of surfactant producers in phytoremediation were described in [109]. It is believed that the most promising for phytoremediation are microorganisms capable of synthesis of surfactant, resistant to metals, as well as those that have been isolated from the rhizosphere of plants [110]. In a series of their investigations, Becerra-Castro et al. [111, 112] reported on the isolation of the metal-resistant microorganisms from the roots of Alyssum serpyllifolium, and 15-20% of them were able to synthesize surfactants.

Limitations and prospects of microbial surfactant using

Most current reviews and experimental papers highlight the positive effects of using microbial surfactants for bioremediation processes, but the critical highlight certain negative aspects of their use will allow us to employ such biotechnology in practice.

The reason of the limited use of microbial surfactants in environmental technologies is that most studies carried out under laboratory conditions, which allow only demonstrate the applicability of certain fundamental approaches [3].

It has to be noted that surfactants using is not always accompanied with enhancing efficiency of remediation: in some cases, positive effects of surfactants were not observed [113, 114]. In addition, the range of studied surfactants is very limited according to their chemical nature and mainly represented by rhamnolipids (Table 3).

The impact of the surfactant concentrations on bioremediation processes is still

insufficiently studied. Most scientists believe that microbial surfactants are non-toxic [95, 96], but on the other hand, they are able to detect antimicrobial properties [115]. In addition, in some cases, the high concentration of surfactant can reduce the speed of the cleaning process, adversely affecting the microorganisms-destructors.

Thus, Whang et al. [116] noted that surfactant at a concentration of 40 mg/l had negative influence on soil remediation of diesel fuel, and at the concentration of 400 mg/l completely inhibited it.

Another important issue of surfactant use in environmental technologies is their biodegradation. On the one hand, this property of microbial surfactants is their advantage over synthetic analogues [95, 96], but on the other — they can be decomposed in the environment quicker than reveal their effect.

Thus, Lin et al. [117] reported that the effectiveness of the remediation significantly increased at the beginning of the experiment, after surfactant introduction, but at the end, results were the same as the controls (without surfactants). It was described phenomenon when rhamnolipids were decomposed faster than diesel fuel, and cleaning did not occur [62, 118].

The scientists associated the solution of this problem with the use of destructors that are not able to use surfactants as a source of carbon [119-121].

In most studies, the scientists use a monoculture of microorganisms-destructors, but more attention is paid to consortia [122]. This is due to the fact that the survival of microorganisms in the composition of consortia is higher compared to monocultures

[123] . It was shown that using of two consortia (composed of the genera Pseudomonas and Bacillus), which form the surfactant, the degree of decomposition of oil in the ground (2%) at the roots of wheat (Triticum aestivum) and mustard (Brassica juncea) was rather high and amounted to 73-75% after 150-180 days

[124] .

Applying consortia in the purification process usually involves bioaugmentation but it depends on many factors: the compatibility of used strains, the ability of strains to synthesize surfactants, etc. In some cases, the addition of the described microorganisms-producers of surfactants had no effect on the cleaning process [125], and competition of few strains for carbon source led to antagonism.

On the other hand, surfactants can contribute to the interaction of microorga-

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Table 6. Stages of development of surfactant biotechnology for environment cleaning [3]

Design step Relevant step Criteria

1 2 3

І. Initial characterization of the polluted area 1. Initial recognition of pollutants Establishment of either single or multi-contaminant type pollution

2. Assessment of the target pollutants concentration range Determination of readily bioavailable, potentially bioavailable and unavailable pollutant fractions

3. Analysis of relevant environmental factors Range of temperature, pH, redox potential, moiety, soil properties, etc.

4. Evaluation of nutrient levels Potential limitation due to insufficient microelements, electron acceptors, etc.

5. Analysis of autochthonous microflora Screening for native microbial consortia with the ability to either remove or mobilize the pollutant by producing biosurfactants

II. Laboratory scale experiments 1. Selection of appropriate bioremediators for conducting the bioremediation process Microorganisms or plants which exhibit high tolerance toward target pollutants and distinct remediation potential (relevant catabolic genes, hyperaccumulative properties, etc.)

2. Selection of additional amendments Nutrients, co-inoculants, plant growth promoting microorganisms, arbuscular mycorrhizal fungi, etc.

А. The economic rationale for the addition of exogenous microbial surfactants (ex situ method) 1. Selection of a biosurfactant and biosurfactant-producing microorganisms Previous studies related to the topic or the native habitat of biosurfactant-producing microorganisms

2. Assessment of potential biosurfactant-induced toxicity EC50 values for relevant bioremediators towards biosurfactant only as well as biosurfactant-pollutant combinations; Analysis of microbial community dynamics as a response to the presence of biosurfactants

3. Evaluation of efficiency for biosurfactant-amended remediation Increase in pollutant bioavailability, increased removal rate, short-term stimulation, enhanced biomass growth for the bioremediator

А. The economic rationale for the addition of exogenous microbial surfactants (ex situ method) 4. Determination of biosurfactant degradability Determination of the period needed for biostimulation of autochthonous microbiota, and the period of surfactant action before its biodegradation

5. Establishment of an optimal biosurfactant production method Cheaper technologies for synthesis of surfactants using waste, the definition of necessity for purification surfactant preparations

В. The economic rationale for the stimulation of surfactant synthesis by autochthonous microbiota (in situ method). 1. Selection of appropriate biosurfactant-producers The choice of destructors from native microbiota that are capable of synthesis of surfactant (native soil microbiota, marine microbiota and rhizobacteria). Using recombinant microorganisms capable of synthesis of surfactants or microbial consortia with high potential of bioaugmentation (relationship between consortium representatives and autochthonous microorganisms)

2. Evaluation of biocompatibility between biosurfactant producers and the biofactor relevant for the treatment process The absence of antagonistic relations, simultaneous growth, increasing bioavailability of pollutants, etc.

3. Selection of an introduction method Introduction of culture fluid or immobilized cells of surfactant producer

4. Initial bioaugmentation tests Absence of negative impact of the producer of surfactants on the balance in the ecosystem and on the native microbiota

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Table 6. End

1 2 3

5. Long-term ability to produce biosurfactants Definition of indicators of surfactant synthesis after introduction, identification of genes responsible for synthesis of surfactants (after a certain period of time)

ІІІ. Field scale feasibility study 1. Environmental response towards biosurfactants or biosurfactant-producers Influence of surfactants and their producers to the microbial balance in the population; surfactant toxicity towards native microbiota, adaptability and survival of the surfactant producer after surfactant introduction, etc.

2. Efficiency of treatment Short-term and long-term removal of target pollutants in biosurfactant-amended treatment compared to control; duration

3. Evaluation of treatment feasibility Justification of each treatment step; Potential Evaluation of treatment feasibility efficiency enhancement vs. additional costs associated with biosurfactant-supplementation

nisms under natural conditions, enhancing the process of xenobiotic degradation (e.g. polyaromatic hydrocarbons). More about this interaction is described in review [113].

It was shown that in case of rhamnolipid introduction, the degree of decomposition of oil containing long-chain n-alkanes and polyaromatic hydrocarbons (PAHs) with a complex structure, by consortium increased by 5.63% [126]. There were no positive effects of surfactants on the efficiency of degradation of oil hydrocarbons in the presence of alkanes with short chains and simple PAHs.

In addition to the introduction of consortia in polluted environment, there is an interesting approach, which involves the selection of autochthonous microbiota and creating recombinant surfactant producers by genetic engineering, followed by the introduction of microorganisms in the ecosystem. However, it is unlikely.

Henry et al. [127] proposed an approach to biostimulation, which means the surfactant introduction in encapsulated form for phenanthrene degradation, but these drugs were less effective than usual.

Concomitant use of bioaugmentation and biostimulation was described in [128, 129]. Angeles et al. [130] studied the decomposition of oil (32 mg/kg) in sterile and non-sterile soil in case of the introduction of P. putida CB-100, capable of synthesis of rhamnolipids. It was found that the introduction of CB-100 strain led to maximum oil degradation in non-sterile soil (61.1%) in the presence of nutrients.

Bioaugmentation was also more effective compared with biostimulation in field studies. Szulc et al. [131] studied the role of

rhamnolipids in the degradation of diesel fuel in the soil during 365 days by a consortium consisting of Aeromonas hydrophila, Alcali-genes xylosoxidans, Gordonia sp., Pseudomonas fluorescens, P. putida, Rhodococcus equi, Stenotrophomonas maltophilia, Xanthomonas.

Llad et al. [132] compared different approaches to improve the efficiency of bioremediation: introduction of mineral substances, rhamnolipids, consortium, destructor fungus Trametes versicolor. It was established that the maximum degree of degradation of hydrocarbons in the soil (50%) was noted after 200 days by adding T. versicolor, which intensified autochthonous microbiota presented by Grampositive bacterial groups of Firmicutes and Actinobacteria.

It should be noted that some authors consider activating autochthonous microbiota ineffective and lengthy process [133].

Efficiency of ecosystem cleaning often depends on the concentration of the limiting factors, including nitrogen, phosphorus and trace elements. It was shown that using mixed cultures, rhamnolipids and additional introduction of nutrients, scientists could reach the degree of decomposition of oil sludge equal 98% for 8 weeks. If nutrients were not used, this figure was only 52% [134]. Similar results were obtained in the case of Lactobacillus delbrueckii [25, 135].

The important problem of remediation is definition of final products of oil degradation. Some authors used Pseudomonas sp., which synthesized surfactants for oil destruction in marine environment (10% volume fraction)

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using GC-MS analysis for the definition of the final products of oil degradation [136]. The schematic representation of possible degradation pathway of crude oil is given at Fig.2.

As for phytoremediation, it remains little known surfactant impact on the plants. In

[137] the authors noted that to remove copper, cadmium and lead, the combined use of Lolium perenne, amino poly carboxylic acid, rhamnolipids and citric acid was quite effective, but surfactants enhanced phytotoxicity. Research of Marecik et al.

[138] confirmed that rhamnolipids highly specifically act on plants, reducing the growth of biomass. Some authors [139] showed that to remove cadmium, phytotoxicity and efficiency of rhamnolipids greatly depend on their concentration. In particular, the concentration of more than 4.4 mmol/kg of surfactants adversely affect the corn and sunflower used in the purification process; and the concentration of 0.02-1.4 mg/kg were ineffective because of sorption in soil matrix.

On the other hand, the success of surfactant using in environmental technologies depends on many factors: pollutant nature, peculiarity of surfactants interaction with the microorganism-destructor or autochthonous microbiota, biodegradation, surfactant toxicity etc. Stages of development of surfactant biotechnology for environment cleaning are presented in Table 6 [3, 140-142].

So, surfactants of different chemical nature and their producers can be used in the processes of soil and water remediation from polyaromatic carbohydrates, petrol carbohydrates, diesel fuel and toxic heavy metals and complex contamination (carbohydrates and metals). Development of effective technologies using microbial surfactants should include the following steps: monitoring of contaminated sites, definition

Crude oil

1

Octadecane

I

3,6-Dimethoxy flourescene

I

Pentadecane

1

Trideca-2,4,6,10-tetraene

Simple end products

Fig. 2. Degradation pathway of crude oil till simple end products [136]

of the nature of pollution and analysis of the autochthonous microbiota; the choice of the microorganism-destructor (according to bioaugmentation process) compatible with natural microbiota; determining the mode of surfactant introduction (exogenous addition of stimulation of surfactant synthesis by autochthonous microbiota); establishing an optimal concentration of surfactant to prevent exhibition of antimicrobial properties and rapid biodegradation; research both in laboratory and field conditions.

REFERENCES

1. Zaki M. S., Fawzi O. M., Abd EL-Zaher M. F. Bioremediation of contaminants. Life Sci. J. 2013, 10 (1), 3329-3332.

2. Tyagi M., da Fonseca M. M., Carvalho C. C. Bioaugmentation and biostimulation strategies to improve the effectiveness of bioremediation processes. Biodegradation. 2011, 22 (2), 231-241.

3. Lawniczak L., Marecik R., Chrzanowski . Contributions of biosurfactants to natural or induced bioremediation. Appl. Microbiol. Biotechnol. 2013, 97 (6), 2327-2339.

4. Das N., Chandran P. Microbial degradation of petroleum hydrocarbon contaminants: an overview. Biotechnol. Res. Int. 2011. doi: 10.4061/2011/941810.

5. Floodgate G. The fate of petroleum in marine ecosystems. In: Atlas R.M., editor. Petroleum Microbiology. New York, USA: Macmillan. 1984, Р.355-398.

6. Bogusiawska-Was E., Dabrowski W. The seasonal variability of yeasts and yeast-like organisms in water and bottom sediment of the Szczecin Lagoon. Int. J. Hyg. Environ. Health. 2001, 203 (5-6), 451-458.

32

Reviews

7. Chaillan F., Le Fleche A., Bury E., Phanta-vong Y. H., Grimont P., Saliot A., Oudot J. Identification and biodegradation potential of tropical aerobic hydrocarbon-degrading microorganisms. Res.Microbiol. 2004, 155 (7), 587-595.

8. Singh H. Mycoremediation: Fungal

Bioremediation. Hoboken: John Wiley & sons, Inc. 2006, 595 р.

9. Ferhat S., Mnif S., Badis A., Eddouaouda K., Alouaoui R., Boucherit A., Mhiri N., Mou-lai-Mostefa N., Sayadi S. Screening and preliminary characterization of biosurfactants produced by Ochrobactrum sp. 1C and Brevibacterium sp. 7 G isolated from hydrocarbon-contaminated soils. Int. Biodeter. Biodegr. 2011, 65 (8), 1182-1188.

10. Shavandi M., Mohebali G., Haddadi A., Shakarami H., Nuhi A. Emulsification potential of a newly isolated biosurfactant-producing bacterium, Rhodococcus sp. strain TA6. Colloids Surf. B. Biointerfaces. 2011, 82 (2), 477-482.

11. Zheng C., Li Z., Su J., Zhang R., Liu C., Zhao M. Characterization and emulsifying property of a novel bioemulsifier by Aeribacillus pallidus YM-1. J.Appl.Microbiol. 2012, 113(1), 44-51.

12. Luna J. M., Rufino R. D., Sarubbo L. A., Campos-Takaki G. M. Characterisation, surface properties and biological activity of a biosurfactant produced from industrial waste by Candida sphaerica UCP0995 for application in the petroleum industry. Colloids Surf. B. Biointerfaces. 2013, 102:202-9. doi: 10.1016/j.colsurfb.2012.08.008.

13. KapadiaSanket G., Yagnik B.N. Current trend and potential for microbial biosurfactants. Asian J. Exp. Biol. Sci. 2013, 4 (1), 1-8.

14. Shoeb E., Akhlaq F., Badar U., Akhter J., Imtiaz S. Classification and industrial applications of biosurfactants. Part-I: Natural and Applied Sciences. Acad. Res. Int. 2013, 4 (3), 243-252.

15. Mukherjee S., Das P., Sen R. Towards commercial production of microbial surfactants. Trends Biotechnol. 2006, 24 (11), 509-515.

16. Mukherjee A. K., Das K. Microbial surfactants and their potential applications: an overview. Adv. Exp. Med. Biol. 2010, V. 672, P. 54-64.

17. Mulligan C. N. Recent advances in the environmental applications of biosurfactants. Curr. Opin. Colloid Interf. Sci. 2009, 14 (5), 372-378.

18. Kosaric N. Biosurfactants and their application for soil bioremediation. Food Technol. Biotechnol. 2001, 39 (4), 295-304.

19. Lai C. C., Huang Y. C., Wei Y. H., Chang J. S. Biosurfactant-enhanced removal of total petroleum hydrocarbons from contaminated soil. J. Hazard Mater. 2009, 167 (1-3), 609-614.

20. Zhang C., Wang S., Yan Y. Isomerization and biodegradation of beta-cypermethrin by Pseudomonas aeruginosa CH7 with biosurfactant production. Bioresource Technol. 2011. 102 (14), 7139-7146.

21. Singh P. B., Sharma S., Saini H. S., Chadha B. S. Biosurfactant production by Pseudomonas sp. and its role in aqueous phase partitioning and biodegradation of chlorpyrifos. Lett. Appl. Microbiol. 2009, 49 (3), 378-383.

22. Sharma S., Singh P., Raj M., Chadha B. S., Saini H. S. Aqueous phase partitioning of hexachlorocyclohexane (HCH) isomers by biosurfactant produced by Pseudomonas aeruginosa WH-2. J. Hazard Mater. 2009, 171 (1-3), 1178-1182.

23. Wattanaphon H. T., Kerdsin A., Thammacha-roen C., Sangvanich P., Vangnai A. S. A biosurfactant from Burkholderia cenocepacia BSP3 and its enhancement of pesticide solubilization. J. Appl. Microbiol. 2008, 105 (2), 416-423.

24. White J. C, Parrish Z. D., Gent M. P., Iannucci-Berger W., Eitzer B. D., Isleyen M., Mattina M. I. Soil amendments, plant age, and intercropping impact p,p’-DDE bioavailability to Cucurbita pepo. J. Environ. Qual. 2006, 35 (4), 992-1000.

25. Thavasi R., Jayalakshmi S., Banat I. M. Application of biosurfactant produced from peanut oil cake by Lactobacillus delbrueckii in biodegradation of crude oil. Bioresource Technol. 2011, 102 (3), 3366-3372.

26. Lakshmi Priya J. Biodegradation of diesel by Aeromonas hydrophila. Int. J. Pharm. Sci. Invent. 2013, 2 (4), 24-36.

27. Mulligan C. N., Gibbs B. F. Types, production and applications of biosurfactants. Proc. Ind. Nat. Sci. Acad. 2004, 70 (1), 31-55.

28. FranzettiA.., Caredda P., Ruggeri C., La Colla P., Tamburini E., Papacchini M., Bestetti G. Potential applications of surface active compounds by Gordonia sp. strain BS29 in soil remediation technologies. Chemosphere. 2009, 75 (6), 801-807.

29. Inakollu S., Hung H., Shreve G. S. Biosurfactant enhancement of microbial degradation of various strructural classes of hydrocarbon in mixed waste systems. Environ. Eng. Sci. 2004, 21 (4), 463-469.

30. Whang L. M., Liu P. W., Ma C. C., Cheng S. S. Application of rhamnolipid and surfactin for enhanced diesel biodegradation - effects of pH and ammonium addition. J. Hazard. Mater. 2009, 164 (2-3), 1045-1050.

31. Cameotra S. S., Singh P. Synthesis of rhamno-lipid biosurfactant and mode of hexadecane uptake by Pseudomonas species. Microbial. Cell Fact. 2009, 8:16. doi: 10.1186/1475-2859-8-16.

32. Al-Tahhan R., Sandrin T. R., Bodour A. A., Maier R. M. Rhamnolipid-iduced removal of lipopolysaccharide from Pseudomonas

33

BIOTECHNOLOGIA ACTA, V. 8, No 4, 2015

aeruginosa: effect on cell surface properties and interaction with hydrophobic substrates. Appl. Environ. Microbiol. 2000, 66 (8), 3262-3268.

33. Sotirova A., Spasova D., Vasileva-Tonkova E, Galabova D. Effects of rhamnolipid-biosurfac-tant on cell surface of Pseudomonas aeruginosa. Microbiol. Res. 2009, 164 (3), 297-303.

34. Mohanty S., Mukherji S. Surfactant aided biodegradation of NAPLs by Burkholderia multivorans: comparison between Triton X-100 and rhamnolipid JBR-515. Colloids Surf. B. Biointerfaces. 2013, 102:644-52. doi: 10.1016/j.colsurfb.2012.08.064.

35. Ron E. Z., Rosenberg E. Biosurfactants and oil bioremediation. Cur. Opin. Biotechnol. 2002, 13 (3), 249-252.

36. Obayori O. S., Ilori M. O., Adebusoye S. A., Oyetibo G. O, Omotayo A. E., Amund O. O. Degradation of hydrocarbons and biosurfactant production by Pseudomonas sp. strain LP1. World J. Microbiol. Biotechnol. 2009, 25 (9), 1615-1623.

37. Reddy M. S., Naresh B., Leela T., Prashanthi M., Madhusudhan N. C., Dhanasri G., Devi P. Biodegradation of phenanthrene with biosurfactant production by a new strain of Brevibacillus sp. Bioresource Technol. 2010, 101 (20), 7980-7983.

38. Kang S. W., Kim Y. B,, Shin J. D., Kim E. K Enhanced biodegradation of hydrocarbons in soil by microbial biosurfactant, sophorolipid. Appl. Biochem. Biotechnol. 2010, 160 (3), 780-790.

39. Das K., Mukherjee A. K. Crude petroleum-oil biodegradation efficiency of Bacillus subtilis and Pseudomonas aeruginosa strains isolated from a petroleum-oil contaminated soil from North-East India. Bioresource Technol. 2007. 98 (7), 1339-1345.

40. Fan M. Y., Xie R. J., Qin G. Bioremediation of petroleum-contaminated soil by a combined system of biostimulation-bioaugmentation with yeast. Environ. Technol. 2014, 35 (1-4), 391-399.

41. Silva E. J., Rocha E., Silva N. M., Rufino R. D., Luna J. M., Silva R. O., Sarubbo L. A. Characterization of a biosurfactant produced by Pseudomonas cepacia CCT6659 in the presence of industrial wastes and its application in the biodegradation of hydrophobic compounds in soil. Colloids Surf. B. Biointerfaces. 117:36-41. doi: 10.1016/j.colsurfb.2014.02.012.

42. Bao M., Pi Y., Wang L., Sun P., Li Y., Cao L. Lipopeptide biosurfactant production bacteria Acinetobacter sp. D3-2 and its biodegradation of crude oil. Environ. Sci. Process Impacts. 2014,16 (4), 897-903. doi: 10.1039/c3em00600j.

43. Das R., Tiwary B. N. Isolation of a novel strain of Planomicrobium chinense from diesel contaminated soil of tropical environment. J. Basic. Microbiol. 2013, 53 (9), 723-732. doi: 10.1002/jobm.201200131.

44. Diab A., El Din S. G. Application of the biosurfactants produced by Bacillus spp. (SH 20 and SH 26) and Pseudomonas aeruginosa SH 29 isolated from the rhizosphere soil of an Egyptian salt marsh plant for the cleaning of oil-contaminataed vessels and enhancing the biodegradation of oily sludge. Afr. J. Environ. Sci. Technol. 2013, 7 (7), 671-679.

45. Saikia R. R., Deka S. Removal of hydrocarbon from refinery tank bottom sludge employing microbial culture. Environ. Sci. Pollut. Res. Int. 2013, 20 (12), 9026-9033. doi: 10.1007/ s11356-013-1888-2.

46. Richlin Machado T., Ajazhajamohideen R., Saravanakumari M., Prabhavathi P. Anti adhesive, antimicrobial and biodegradability assay of a lipopeptide biosurfactant from Lactococus lactis. Int. J. Sci. Innovat. Discover. 2013, 3 (4), 478-483.

47. Li C., Zhou Z. X., Jia X. Q., Chen Y., Liu J., Wen J. P. Biodegradation of crude oil by a newly isolated strain Rhodococcus sp. JZX-01. Appl. Biochem. Biotechnol. 2013, 171 (7), 1715-1725. doi: 10.1007/s12010-013-0451-4.

48. Jain R. M., Mody K., Joshi N., Mishra A, Jha B. Effect of unconventional carbon sources on biosurfactant production and its application in bioremediation. Int. J. Biol. Macromol. 2013, 62:52-8. doi: 10.1016/j. ijbiomac.2013.08.030.

49. Pandey A. K., Chaudhary P., Singh S. B., Arora A., Kumar K., Chaudhry S., Nain L. Deciphering the traits associated with PAH degradation by a novel Serratia marcesencs L-11 strain. J. Environ. Sci. Health. A. Tox. Hazard. Subst. Environ. Eng. 2012, 47 (5), 755-765 doi: 10.1080/10934529.2012.660108.

50. Urum K., Grigson S., Pekdemir T., McMena-my S. A comparison of the efficiency of different surfactants for removal of crude oil from contaminated soils. Chemosphere. 2006, 62 (9), 1403-1410.

51. Mnif I., Sahnoun R., Ellouze-Chaabouni S., Ghribi D. Evaluation of B. subtilis SPB1 biosurfactants’ potency for diesel-contaminated soil washing: optimization of oil desorption using Taguchi design. Environ. Sci. Pollut. Res. Int. 2014, 21 (2), 851-861. doi: 10.1007/s11356-013-1894-4.

52. Kildisas V., Levisauskas D., Grigiskis S. Development of clean-up complex technology of soil contaminated by oil pollutants based on cleaner production concepts. Environ. Res. Eng. Manage. 2003, 25 (3), 87-93.

53. Baskys E., Grigiskis S., Levisauskas D,, Kildisas V. A new complex technology of clean-up of soil contaminated by oil pollutants. Environ. Res. Eng. Manage. 2004, 30 (4), 78-81.

54. Moldes A. B., Paradelo R., Rubinos D., Devesa-Rey R., Cruz J. M., Barral M. T. Ex situ treatment of hydrocarbon-contaminated

34

Reviews

soil using biosurfactants from Lactobacillus pentosus. J. Agr. Food Chem. 2011, 59 (17), 9443-9447.

55. Moldes B., Paradelo R., Vecino X., Cruz J. M., Gudina E., Rodrigues L., Teixeira J. A., Dominguez J. M., Barral M. T. Partial characterization of biosurfactant from Lactobacillus pentosus and comparison with sodium dodecyl sulphate for the bioremediation of hydrocarbon contaminated soil. Biomed. Res. Int. 2013, 2013:961842. doi: 10.1155/2013/961842.

56. Manickam N., Bajaj A., Saini H. S., Shanker R. Surfactant mediated enhanced biodegradation of hexachlorocyclohexane (HCH) isomers by Sphingomonas sp. NM05. Biodegradation. 2012, 23 (5), 673-682.

57. Jorfi S., Rezaee A., Mobeh-Ali G.-A., Jaafarzadeh N. A. Application of biosurfactants produced by Pseudomonas aeruginosa SP4 for bioremediation of soils contaminated by pyrene. Soil Sediment Contam. 2013, 22 (8), 890-911. doi:10.1080/15320383.2013.77043.

58. Timma L., Sams K., Valtere S., Vilgerts J., Blumberga D. Full factorial design of screening experiments for biosurfactant enhanced remediation of hydrophobic substances in soil. J. Clean Energy Technol. 2014, 2 (1), 51-56.

59. Sobrinho H. B. S., de Luna J. M., Rufino R. D., Porto A. L. F., Sarubbo L. A. Application of biosurfactant from Candida sphaerica UCP 0995 in removal of petroleum derivative from soil and sea. Water J. Life Sci. 2013, 7 (6), 559-569.

60. Cerqueira V. S., Hollenbach E. B., Maboni F., Camargo F. A., Peralba Mdo C, Bento F. M. Bio-prospection and selection of bacteria isolated from environments contaminated with petrochemical residues for application in bioremediation. World J. Microbiol. Biotechnol. 2012, 28 (3), 1203-1222. doi: 10.1007/s11274-011-0923-z.

61. Meyer D. D., Santestevan N. A., Bucker F.,

Salamoni S. P., Andreazza R., De Oliveira Camargo F. A., Bento F. M. Capability of a selected bacterial consortium for degrading diesel/biodiesel blends (B20): enzyme and biosurfactant production. J. Environ. Sci. Health. A. Tox. Hazard. Subst. Environ. Eng. 2012, 47 (12), 1776-1784. doi:

10.1080/10934529.2012.689227.

62. Chrzanowski L., Dziadas M., Lawniczak L., Cyplik P., Bialas W., Szulc A., Lisiecki P., Jelen H. Biodegradation of rhamnolipids in liquid cultures: effect of biosurfactant dissipation on diesel fuel/B20 blend biodegradation efficiency and bacterial community composition. Bioresour. Technol. 2012, 111:328-35. doi: 10.1016/j.biortech.2012.01.181.

63. Pei X.-H., Zhan X.-H., Wang S.-M., Lin Y.-S., Zhou L.-X. Effects of a biosurfactant and a synthetic surfactant on phenanthrene degradation by a Sphingomonas strain. Pedosphere. 2010, 20 (6), 771-779.

64. Cui C. Z,, Zeng C, Wan X,, Chen D,, Zhang J. Y., Shen P. Effect of rhamnolipids in degradation of anthracene by two newly isolated strains, Sphingomonas sp. 12A and Pseudomonas sp. 12B. J. Microbiol. Biotechnol. 2008, 18 (1), 63-66.

65. Zeng G., Liu Z., Zhong H., Li J., Yuan X., Fu H., Ding Y., Wang J., Zhou M. Effect of monorhamnolipid on the degradation of n-hexadecane by Candida tropicalis and the association with cell surface properties. Appl. Microbiol. Biotechnol. 2011, 90 (3), 11551161. doi: 10.1007/s00253-011-3125-6.

66. Husain S. Effect of surfactants on pyrene degradation by Pseudomonas fluorescens 29 L. World J. Microbiol. Biotechnol. 2008, 24 (11), 2411-2419.

67. Zhang J., Yin R., Lin X., Liu W., Chen R., Li X. Interactive effect of biosurfactant and microorganism to enhance phytoremediation for removal of aged polycyclic aromatic hydrocarbons from contaminated soils. J. Health Sci. 2010, 56 (3), 257-266.

68. Liu Z.-F., Zeng G.-M., Wang J., Zhong H., Ding Y., Yuan X.-Z. Effects of mono-rhamnolipid and Tween 80 on the degradation of phenol by Candida tropicalis. Process Biochem. 2010, 45 (5), 805-809.

69. McKew B. A., Coulon F., Yakimov M. M., Dena-ro R., Genovese M., Smith C. J., Osborn A. M., Timmis K. N., McGenity T. J. Efficacy of intervention strategies for bioremediation of crude oil in marine systems and effects on indigenous hydrocarbonoclastic bacteria. Environ. Microbiol. 2007, 9 (6), 1562-1571.

70. Nikolopoulou M., Kalogerakis N. Enhanced

bioremediation of crude oil utilizing lipophilic fertilizers combined with biosurfactants and molasses. Mar. Pollut. Bull. 2008, 56 (11), 1855-1861. doi:

10.1016/j.marpolbul.2008.07.021.

71. Gottfried A., Singhal N., Elliot R., Swift S. The role of salicylate and biosurfactant in inducing phenanthrene degradation in batch soil slurries. Appl. Microbiol. Biotechnol. 2010, 86 (5), 1563-1571.

72. Shin K. H., Kim K. W., Ahn Y. Use of biosurfactant to remediate phenanthrene-contaminated soil by the combined solubilization biodegradation process. J. Hazard. Mater. 2006, 137 (3), 1831-1837.

73. Owsianiak M., Chrzanowski L., Szulc A., Staniewski J., Olszanowski A., Olejnik-Schmidt A. K., Heipieper H. J. Biodegradation of diesel/biodiesel blends by a consortium of hydrocarbon degraders: Effect of the type of blend and the addition of biosurfactants. Bioresour. Technol. 2009, 100 (3), 14971500. doi: 10.1016/j.biortech.2008.08.028.

74. Owsianiak M., Szulc A., Chrzanowski L., Cyplik P., Bogacki M., Olejnik-Schmidt A. K., Heipieper H. J. Biodegradation and

35

BIOTECHNOLOGIA ACTA, V. 8, No 4, 2015

surfactant-mediated biodegradation of diesel fuel by 218 microbial consortia are not correlated to cell surface hydrophobicity. Appl. Microbiol. Biotechnol. 2009, 84 (3), 545-553. doi: 10.1007/s00253-009-2040-6.

75. Cerqueira V. S ., Hollenbach E. B., Maboni F., Vainstein M. H, Camargo F. A. O., Peral-ba M. D. C. R, Bento F. M. Biodegradation potential of oily sludge by pure and mixed bacterial cultures. Bioresour. Technol. 2011, 102 (23), 11003-11010. doi: 10.1016/j. biortech.2011.09.074.

76. Martins V. G., Kalil S. J, Costa J. A. V. In situ bioremediation using biosurfactant produced by solid state fermentation. World J. Microb. Biot. 2009, 25 (5), 843-851.

77. Das K., Mukherjee A. K. Differential utilization of pyrene as the sole source of carbon by Bacillus subtilis and Pseudomonas aeruginosa strains: Role of biosurfactants in enhancing bioavailability. J. Appl. Microbiol. 2007, 102 (1), 195-203.

78. Gao L., Kano N., Sato Y., Li C, Zhang S, Imaizumi H. Behavior and distribution of heavy metals including rare earth elements, thorium, and uranium in sludge from industry water treatment plant and recovery method of metals by biosurfactants application. Bioinorg. Chem. Appl. 2012, 2012:173819. doi: 10.1155/2012/173819.

79. Singh P., Cameotra S. S. Enhancement of metal bioremediation by use of microbial surfactants. Biochem. Biophys. Res. Commun. 2004, 319 (2), 291-297.

80. Pacwa-Plociniczak M, Plaza G. A., Piotrow-ska-Seget Z., Cameotra S. S. Environmental applications of biosurfactants: recent advances. Int. J. Mol. Sci. 2004, 12 (1), 633-654.

81. J uwarkarAA., NairA, Dubey K. V., Singh S. K, Devotta S. Biosurfactant technology for remediation of cadmium and lead contaminated soils. Chemosphere. 2007, 68 (10), 1996-2002.

82. A$ci Y., Nurba§ M., Acikel Y. S. A comparative study for the sorption of Cd(II) by soils with different clay contents and mineralogy and the recovery of Cd(II) using rhamnolipid biosurfactant. J. Hazard. Mater. 2008, 154 (1-3), 663-673.

83. Mulligan C. N. Environmental applications for biosurfactants. Environ. Pollut. 2005, 133 (2), 183-198.

84. Juwarkar A.A., Dubey K. V., NairA., Singh S. K. Bioremediation of multi-metal contaminated soil using biosurfactant — a novel approach. Ind. J. Microbiol. 2008, 48 (1), 142-146.

85. Das P., Mukherjee S., Sen R. Biosurfactant of marine origin exhibiting heavy metal remediation properties. Bioresource Technol. 2009, 100 (20), 4887-4890.

86. Liu X., WangJ. T., ZhangM., Wang L., YangY. T. Remediation of Cu-Pb-contaminated loess

soil by leaching with chelating agent and biosurfactant. Huan. Jing. Ke. Xue. 2013, 34 (4), 1590-1597.

87. Cao M., Hu Y., Sun Q., Wang L., Chen J., Lu X.

Enhanced desorption of PCB and trace metal elements (Pb and Cu) from contaminated soils by saponin and EDDS mixed solution. Environ. Pollut. 2013, 174:93-9. doi:

10.1016/j.envpol.2012.11.015.

88. Dahrazma B., Mulligan C. N. Investigation of the removal of heavy metals from sediments using rhamnolipid in a continuous flow configuration. Chemosphere. 2007, 69 (5), 705-711.

89. Wang S., Mulligan C. N. Rhamnolipid foam enhanced remediation of cadmium and nickel contaminated soil. Water Air Soil Pollut. 2004, 157 (1), 315-330.

90. Maity J. P., Huang Y. M., Hsu C. M., Wu C. I., Chen C. C., Li C. Y., Jean J. S., Chang Y. F., Chen C. Y. Removal of Cu, Pb and Zn by foam fractionation and a soil washing process from contaminated industrial soils using soapberry-derived saponin: a comparative effectiveness assessment. Chemosphere. 2013, 92 (10), 1286-1293. doi: 10.1016/j. chemosphere.2013.04.060.

91. Ayci Y., Nurba§ M., Acikel Y. S. Investigation of sorption/desorption equilibria of heavy metal ions on/from quartz using rhamnolipid biosurfactant. J.Environ.Manage. 2010, 91 (3), 724-731. doi: 10.1016/j.jenvman.2009.09.036.

92. Karwowskaa E., Andrzejewska-Morzucha D., Lebkowskaa M., Tabernackaa A., Wojtkows-kab M., Telepkob A., Konarzewska A. Bioleaching of metals from printed circuit boards supported with surfactant-producing bacteria. J. Hazard. Mater. 2014, 264:20310. doi: 10.1016/j.jhazmat.2013.11.018.

93. Olaniran A. O., Balgobind A., Pillay B. Bioavailability of heavy metals in soil: impact on microbial biodegradation of organic compounds and possible improvement strategies. Int. J. Mol. Sci. 2013, 14 (5), 10197-10228. doi: 10.3390/ijms140510197.

94. Sandrin T. R., Maier R. M. Impact of metals on the biodegradation of organic pollutants. Environ.. Health.. Perspect. 2003, 111 (8), 1093-1101.

95. Lima T. M. S., Procopio L. C., Brandao F. D., Carvalho A. M. X., Totola M. R., Borges A. C. Biodegradability of bacterial surfactants. Biodegradation. 2011, 22 (3), 585-592.

96. Lima T. M. S., Procopio L. C., Brandao F. D., Carvalho A. M. X., Totola M. R., Borges A. C. Simultaneous phenanthrene and cadmium removal from contaminated soil by a ligand/ biosurfactant solution. Biodegradation. 2011, 22 (5), 1007-1015. doi: 10.1007/s10532-011-9459-z.

97. Lima T. M. S., Procopio L. C., Brandao F. D., Leao B.A., Totola M. R., Borges A. C. Evaluation of bacterial surfactant toxicity towards

36

Reviews

petroleum degrading microorganisms. Bioresource Technol. 2011, 102 (3), 29572964. doi: 10.1016/j.biortech.2010.09.109.

98. Sandrin T. R., Chech A. M., Maier R. M. A rhamnolipid biosurfactant reduces cadmium toxicity during napthalene biodegradation. Appl. Environ. Microbiol. 2000. 66 (10), 4585-4588.

99. Maslin P. M., Maier R. M. Rhamnolipid enhanced mineralization of phenanthrene in organic metal co-contaminated soils. Bioremed. J. 2000, 4 (4), 295-308.

100. Singh A. K., Cameotra S. S. Efficiency of lipopeptide biosurfactants in removal of petroleum hydrocarbons and heavy metals from contaminated soil. Environ. Sci. Pollut. Res. Int. 2013, 20 (10), 7367-7376. doi: 10.1007/s11356-013-1752-4.

101. Chrzanowski L., Wick L. Y., Meulenkamp R., Kaestner M., Heipieper H. J. Rhamnolipid biosurfactants decrease the toxicity of chlorinated phenols to Pseudomonas putida DOT-T1E. Lett. Appl. Microbiol. 2009, 48 (6), 756-762.

102. Chrzanowski T., Owsianiak M., Szulc A., Marecik R., Piotrowska-Cyplik A., Olejnik-Schmidt A. K., Staniewski J., Lisiecki P., Ciesielczyk F., Jesionowski T., Heipieper H. J. Interactions between rhamnolipid biosurfactants and toxic chlorinated phenols enhance biodegradation of a model hydrocarbon-rich effluent. Int. Biodeter. Biodegr. 2011, 65 (4), 605-611.

103. Nievas M. L., Commendatore M. G., Este-vas J. L., Bucala V. Biodegradation pattern of hydrocarbons from a fuel oil-type complex residue by an emulsifier-producing microbial consortium. J. Hazard. Mater. 2008, 157 (1-3), 96-104.

104. Mirza N., Mahmood Q., Maroof Shah M., Pervez A., Sultan S. Plants as useful vectors to reduce environmental toxic arsenic content. Scientific World J. 2014, 2014:921581. doi: 10.1155/2014/921581.

105. Bell T. H., Joly S., Pitre F. E., Yergeau E. Increasing phytoremediation efficiency and reliability using novel omics approaches. Trends Biotechnol. 2014, 32 (5), 271-280. doi: 10.1016/j.tibtech.2014.02.008.

106. Halaimi F. Z., Kellali Y., Couderchet M.,

Semsari S. Comparison of biosorption and phytoremediation of cadmium and methyl parathion, a case-study with live Lemna gibba and Lemna gibba powder. Ecotoxicol. Environ. Saf. 2014, 105:112-20. doi:

10.1016/j.ecoenv.2014.02.002.

107. Kamran M. A., Amna Mufti R., Mubariz N., Syed J. H., Bano A., Javed M. T., Munis M. F., Tan Z., Chaudhary H. J. The potential of the flora from different regions of Pakistan in phytoremediation: a review. Environ. Sci. Pollut. Res. Int. 2014, 21 (2), 801-812. doi: 10.1007/s11356-013-2187-7.

108. Sheng X., He L., Wang Q., Ye H., Jiang C. Effects of inoculation of biosurfactant-producing Bacillus sp. J119 on plant growth and cadmium uptake in a cadmium-amended soil. J. Hazard. Mater. 2008, 155 (1-2), 17-22.

109. Lebeau T., Braud A., Jezequel K. Performance of bioaugmentation-assisted phytoextraction applied to metal contaminated soils: a review. Environ. Pollut. 2008, 153 (3), 497-522.

110. Lodewyckx C., Mergeay M., Vangronsveld J., Clijsters H., Van Der Lelie D. Isolation, characterization, and identification of bacteria associated with the zinc hyperaccumulator Thlaspi cae ru les cens subsp. Calaminaria. Int. J. Phytoremediation. 2002, 4 (2), 101-115.

111. Becerra-Castro C., Prieto-Fernandez A., Alvarez-Lopez V., Monterroso C., Cabel-lo-Conejo M. I., Acea M. J., Kidd P. S. Nickel solubilizing capacity and characterization of rhizobacteria isolated from hyperac-cumulating and non-hyperaccumulating subspecies of alyssum serpyllifolium. Int. J. Phytoremediation. 2011, 13 (Suppl. 1), 229-244.

112. Becerra-Castro C., Monterroso C., Prieto-Fernandez A., Rodriguez-Lamas L., Loureiro-Vinas M., Acea M. J., Kidd P. S. Pseudometallophytes colonising Pb/Zn mine tailings: A description of the plant-microorganism-rhizosphere soil system and isolation of metal-tolerant bacteria. J. Hazard. Mater. 2012, 217-218:350-9. doi: 10.1016/j.jhazmat.2012.03.039.

113. McGenity T. J., Folwell B. D., McKew B. A., Sanni G. O. Marine crude-oil biodegradation: a central role for interspecies interactions. Aquat. Biosyst. 2012, 8(1):10. doi: 10.1186/2046-9063-8-10.

114. Bayer D. M., Chagas-SpinelliA. C., Gavazza S., Florencio L., Kato M. T. Natural attenuation and biosurfactant-stimulated bioremediation of estuarine sediments contaminated with diesel oil. Appl. Biochem. Biotechnol. 2013, 171 (1), 173-188. doi: 10.1007/s12010-013-0358-0.

115. Vatsa P., Sanchez L., Clement C., Baillieul F., Dorey S. Rhamnolipid biosurfactants as new players in animal and plant defense against microbes. Int. J. Mol. Sci. 2010, 11 (12), 5095-5108. doi: 10.3390/ijms11125095.

116. Whang L. M,, Liu P. W., Ma C. C., Cheng S. S. Application of biosurfactants, rhamnolipid, and surfactin, for enhanced biodegradation of diesel-contaminated water and soil. J. Hazard. Mater. 2008, 151 (1), 155-163.

117. Lin T. C., Pan P. T., Young C. C., Chang J. S., Chang T. C., Cheng S. S. Evaluation of the optimal strategy for ex situ bioremediation of diesel oil-contaminated soil. Environ. Sci. Pollut. Res. Int. 2011, 18 (9), 1487-1496. doi: 10.1007/s11356-011-0485-5.

118. Chrzanowski L., Lawniczak L., Czaczyk K. Why do microorganisms produce rhamno-

37

BIOTECHNOLOGIA ACTA, V. 8, No 4, 2015

lipids? World J. Microbiol. Biotechnol. 2012, 28 (2), 401-419.

119. Hidayati N. V., Hilmi E., Haris A., Effendi H., Guiliano M., Doumenq P., Syakti A. D. Fluorene removal by biosurfactants producing Bacillus megaterium. Waste Biomass Valor. 2011, 2 (4), 415-422.

120. Tzintzun-Camacho O, Loera O, Ramirez-Saad H. C., Gutierrez-Rojas M. Comparison of mechanisms of hexadecane uptake among pure and mixed cultures derived from a bacterial consortium. Int. Biodeter. Biodegr. 2012, 70. doi:10.1016/j.ibiod.2012.01.009.

121. Saimmai A., Kaewrueng J., Maneerat S. Used lubricating oil degradation and biosurfactant production by SC-9 consortia obtained from oil-contaminated soil. Ann. Microbiol. 2012, 62 (4), 1757-1767.

122. Kadali K. K., Simons K. L., Sheppard P. J., Ball A. S. Mineralisation of weathered crude oil by a hydrocarbonoclastic consortia in marine mesocosms. Water Air Soil Poll. 2012, 223 (7), 4283-4295.

123. Sampath R., Venkatakrishnan H., Ravichan-dran V., Chaudhury R. R. Biochemistry of TBT-degrading marine Pseudomonads isolated from Indian coastal water. Water Air Soil Poll. 2012, 223 (1), 99-106.

124. Kumar R., Bharagava R. N., Kumar M., Singh S. K., Govind K. Enhanced Biodegradation of mobil oil hydrocarbons by biosurfactant producing bacterial consortium in wheat and mustard rhizosphere. Pet. Environ. Biotechnol. 2013, 4:5. http:// dx.doi.org/10.4172/2157-7463.1000158.

125. Sun G. D., Xu Y,, Jin J. H., Zhong Z. P,, Liu Y., Luo M., Liu Z. P. Pilot scale ex-situ bioremediation of heavily PAHs-contaminated soil by indigenous microorganisms and bioaugmentation by a PAHs-degrading and bioemulsifier-producing strain. J. Hazard. Mater. 2012, 233-234:72-8. doi: 10.1016/j. jhazmat.2012.06.060.

126. Chen Q., Bao M., Fan X., Liang S., Sun P. Rhamnolipids enhance marine oil spill bioremediation in laboratory system. Mar. Pollut. Bull. 2013, 71 (1-2), 269-275. doi: 10.1016/j.marpolbul.2013.01.037.

127. Henry N. D., Robinson L., Johnson E., Cherrier J., Abazinge M. Phenanthrene emulsification and biodegradation using rhamnolipid biosurfactants and Acineto bac-ter calcoaceticus in vitro. Bioremed. J. 2011, 15 (2), 109-120.

128. Lin T. C., Pan P. T., Cheng S. S. Ex situ bioremediation of oil-contaminated soil. J. Hazard. Mater. 2010, 176 (1-3), 27-34. doi: 10.1016/j.jhazmat.2009.10.080.

129. Turgay O. C., Erdogan E., Karaca A. Effect of humic deposit (leonardite) on degradation of semi-volatile and heavy hydrocarbons and

soil quality in crude-oil-contaminated soil. Environ. Monit.Assess. 2010, 170 (1-4), 4558. doi: 10.1007/s10661-009-1213-1.

130. A ngeles M. T., Refugio R. V.In situ biosurfactant production and hydrocarbon removal by Pseudomonasputida CB-100 in bioaugmented and biostimulated oil-contaminated soil. Braz. J.Microbiol. 2013, 44 (2), 595-605. doi: 10.1590/S1517-83822013000200040.

131. Szulc A., Ambrozewicz D., Sydow M., Law-niczak L., Piotrowska-Cyplik A., Marecik R., Chrzanowski L. The influence of bioaugmentation and biosurfactant addition on bioremediation efficiency of diesel-oil contaminated soil: Feasibility during field studies. J.Environ.Manage. 2014, 132:1218. doi: 10.1016/j.jenvman.2013.11.006.

132. Llado S., Solanas A. M., de Lapuente J.,

Borras M., Vinas M. A diversified approach to evaluate biostimulation and bioaugmentation strategies for heavy-oil-contaminated soil. Sci. Total. Environ. 2012, 435-436:262-9. doi: 10.1016/j.

scitotenv.2012.07.032.

133. Dindar E., §agban F. O. T., Ba§kaya H. S. Bioremediation of petroleum-contaminated soil. J. Biol. Env. Sci. 2013, 7 (19), 39-47.

134. Cameotra S. S., Singh P. Bioremediation of oil sludge using crude biosurfactants. Int. Biodeter. Biodegr. 2008, 62 (3), 274-280.

135. Thavasi R., Jayalakshmi S., Banat I. M. Effect of biosurfactant and fertilizer on biodegradation of crude oil by marine isolates of Bacillus megaterium, Corynebacterium kutscheri and Pseudomonas aeruginosa. Bioresource Technol. 2011, 102 (2), 772778. doi: 10.1016/j.biortech.2010.08.099.

136. Saravana Kumari P., Amruta S. R. Analysis of biodegradation pathway of crude oil by Pseudomonas sp. isolated from marine water sample. Arch. Appl. Sci. Res. 2013, 5 (4), 165-171.

137. Gunawardana B., Singhal N., Johnson A. Amendments and their combined application for enhanced copper, cadmium, lead uptake by Lolium perenne. Plant Soil. 2010, 329 (1-2), 283-294.

138. Marecik R., Wojtera-Kwiczor J .,LawniczakL., Cyplik P., Szulc A., Piotrowska-Cyplik A., Chrzanowski L. Rhamnolipids increase the phytotoxicity of diesel oil towards four common plant species in a terrestrial environment. Water Air Soil Pollut. 2012, 223 (7), 4275-4282.

139. Wen J., McLaughlin M. J., Stacey S. P., Kirby J. K. Is rhamnolipid biosurfactant useful in cadmium phytoextraction? J. Soils Sediments. 2010, 10 (7), 1289-1299.

140. Bhavani T. M. B., Hemashenpagam N. Production of biosurfactant and characterization by 16S rRNA sequencing

38

Reviews

technique of bacteria degrading hydrocarbon isolatedfrom petroleum contaminated sites. Int. J. Adv. Res. 2013, 1 (5), 300-305.

141. Amit P.,Ayush S. Production of biosurfactant from Bacillus megaterium and Pseudomonas fluorescenes isolated from oil contaminated sources and expression of biosurfactant

producing genes. World J. Pharm. Pharmac. Sci. 2013, 2 (5), 2765-2788.

142. Phan C.-W., Bakar N. F. A., Hamzah A A Comparative study on biosurfactant activity of crude oil-degrading bacteria and its correlation to total petroleum hydrocarbon degradation. Bioremed. J. 2013, 17 (4), 240-251.

МІКРОБНІ ПОВЕРХНЕВО-АКТИВНІ РЕЧОВИНИ У ПРИРОДООХОРОННИХ ТЕХНОЛОГІЯХ

Т. П. Пирог А. Д. Конон І. В. Савенко

Національний університет харчових технологій, Київ, Україна

E-mail: [email protected]

В огляді наведено дані літератури та власних експериментальних досліджень авторів щодо використання мікробних гліколіпідів (рамно-, софоро- і трегалозоліпідів) та ліпопеп-тидів для очищення води і ґрунту від нафти та інших вуглеводнів, вилучення токсичних важких металів (Cu2+, Cd2+, Ni2+, Pb2+), деструкції комплексних забруднень (нафта й інші вуглеводні з важкими металами), а також висвітлено роль мікробних поверхнево-активних речовин у процесах фіторемедіації.

Обговорюються чинники, що обмежують використання мікробних поверхнево-активних речовин у природоохоронних технологіях. За певних концентрацій поверхнево-активні речовини можуть виявляти антимікробні властивості та інгібувати мікроорганізми-декс-труктори ксенобіотиків. Біодеградабельність таких речовин може також знижувати ефективність біоремедіації.

Розроблення ефективної технології з використанням мікробних поверхнево-активних речовин має включати такі етапи: моніторинг забрудненої ділянки, з’ясування характеру забруднення і аналіз автохтонної мікробіоти; визначення способу введення поверхнево-активних речовин (екзогенне внесення, стимуляція їх синтезу автохтонною мікробіотою); встановлення оптимальної концентрації для уникнення вияву антимікробних властивостей, а також швидкої біодеградації; проведення досліджень як у лабораторних, так і в польових умовах.

Ключові слова: мікробні поверхнево-активні речовини, біоремедіація.

МИКРОБНЫЕ ПОВЕРХНОСТНОАКТИВНЫЕ ВЕЩЕСТВА В ПРИРОДООХРАННЫХ ТЕХНОЛОГИЯХ

Т. П. Пирог А. Д. Конон И. В. Савенко

Национальный университет пищевых технологий, Киев, Украина

E-mail: [email protected]

Представлены данные литературы и собственных экспериментальных исследований авторов о применении микробных поверхностно-активных гликолипидов (рамно-, софоро- и трегалозолипидов) и липопептидов для очистки воды и почвы от нефти и других углеводородов, удаления токсичных тяжелых металлов (Cu2+, Cd2+, Ni2+, Pb2+), деструкции комплексных загрязнений (нефть и другие углеводороды с тяжелыми металлами), а также освещена роль микробных поверхностно-активных веществ в процессах фиторемедиации.

Обсуждаются факторы, ограничивающие использование микробных поверхностно-активных веществ в природоохранных технологиях. При определенных концентрациях поверхностно-активные вещества могут проявлять антимикробные свойства и ингибировать микроорганизмы-декструкторы ксенобиотиков. Биодеградабельность сурфактантов микроорганизмами также может снижать эффективность биоремедиации.

Разработка эффективной технологии с использованием микробных поверхностно-активных веществ должна включать следующие этапы: мониторинг загрязненного участка, определение характера загрязнения и анализ автохтонной микробиоты; определение способа введения поверхностно-активных веществ (экзогенное внесение, стимуляция их синтеза автохтонной микробиотой); установление оптимальной концентрации для предотвращения проявления антимикробных свойств, а также быстрой биодеградации; проведение исследований как в лабораторных, так и в полевых условиях.

Ключевые слова: микробные поверхностноактивные вещества, биоремедиация.

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