Long-Term Combined Effects of Crude Oil and Dispersant on Sediment Bacterial Community

Journal of Environmental Treatment Techniques

2021, Volume 9, Issue 1, Pages: 259-263

J. Environ. Treat. Tech.

ISSN: 2309-1185

Journal web link: http://www.jett.dormaj.com

https://doi.org/10.47277/JETT/9(1)263

Long-Term Combined Effects of Crude Oil and

Dispersant on Sediment Bacterial Community

Mohammed Al-Jawasim*

Department of Environmental Science/ University of Al-Qadisiyah, Al-Dewaniya, 58014, Iraq

Received: 16/08/2020

Accepted: 13/11/2020

Published: 20/03/2021

Abstract

To better understand long-term combined effects of crude oil and dispersant on bacterial community, sediments microcosms were

set up in triplicates and treated with dispersant (Corexit 9500A), crude oil, and Corexit 9500A plus crude oil. After 60 days exposure,

there was a significant change in the bacterial community structure in all treatments. The shift in the bacterial community structure in

Corexit 9500A plus crude oil treatment was considerably different from those by either Corexit 9500A or crude oil. DNA sequence

analysis showed that Hydrocarboniphaga effuse, Parvibaculum lavamentivorans,and Alicyclobacillus ferrooxydans were the major

bacterial species in crude oil treatment. Pandoraea thiooxydans, Janthinobacterium sp. and Hyphomicrobium nitrativorans were the

most dominant species in Corexit 9500A treatment. The species Janthinobacterium sp., Parvibaculum lavamentivorans, and Dyella sp.

were enriched in Corexit 9500A plus crude oil treatment. The majority of the detected species were hydrocarbons degraders. The study

showed that Corexit 9500Aaddition enhanced the biodegradation rate by increasing the diversity and richness of hydrocarbons degrading

species. Corexit A9500 application should be considered during crude oil spills to evaluate environmental impacts.

Keywords: Corexit A9500, crude oil, combined effects, bacterial community structure, hydrocarbons

oil bioavailability to indigenous oil degrading microbes and

Introduction

consequently increase crude oil biodegradation rate [1, 2]. A

study found the number of hydrocarbon-degrading

microorganisms and the total carbon mineralization are being

increased by the chemical dispersant Corexit 9500A [12].

Another study demonstrated that approximately 60% of crude

oil was degraded after Corexit 9500A treatment [13]. It was

found that the biodegradation rate of crude oil increased in

response to Corexit 9500A addition [11]. The short exposure

period (7 days) to crude oil and Corexit 9500A plus crude oil

exert no impact on the bacterial community [14]. The

objectives of this research are to examine the combined effects

of Corexit 9500Aplus crude oil after 60 days incubation and to

identify the bacterial taxa that dominate the bacterial

community under these conditions.

Crude oil is a complex mixture of various organic and

inorganic compounds including hydrocarbons, resins, and

asphaltenes. Crude oil is released into marine environments by

natural and anthropogenic activities, which contribute up to

3% of entire oil spills [1]. Oil spills severely impact

ecosystems and cause long-term environmental damages [2],

ranging from molecular to organismal levels [3].

Bioremediation is

process that employs natural

microorganisms to break down complex toxic compounds to

less toxic or non-toxic compounds. Microorganism uses

pollutants as sole sources of energy and consequently break

them from toxic compounds to benign wastes that have no

harmful effects on the environment. Due to its high selectivity

and specificity of removing pollutants, cost efficiency, and less

installing requirements, the bioremediation process is preferred

over other physiochemical methods. Pollutants generally

increase the microbial lag phase and therefore reduce the

biodegradation rate [4]. Bioremediation is affected by a number

of factors such as presence of appropriate biodegrading-

organisms, the concentration of contaminants, and nutrients

bioavailability temperature, oxygen, pH, degree of acclimation,

cellular transport properties and chemical structure of the

compound [5]; therefore, bioremediation occurs on a relatively

slow rate [6].

Dispersant application is one of the strategies that have

been employed since the 1950s to mitigate oil spill impacts on

aquatic environments [7]. Dispersants are mixtures of

surfactants, solvents, and other compounds [8, 9]. Dispersants

break up oil slicks into micron-sized droplets by reducing the

interfacial tension at oil-water interfaces [9, 10, 11]. The

droplets spread in the water column inhibiting surface oil slicks

formation. Breaking down oil slicks into tiny droplets increases

2 Materials and Methods

2.1 Study area

The study area was a salt marsh at the eastern side of Lake

Pontchartrain, Louisiana (N30º 08.782’ W89º 44.665’). The

marsh was dominated by two marsh plants species Spartina

patens and S. alterniflora. After removing the surface plants,

the top 30 cm of sediments was collected. The sample was kept

in sterilized polyethylene containers, sent on ice to the Troy

University/Department of Biological and Environmental

Science's laboratory, and stored at 4°C before analysis.

2.2 Chemical analyses

Chemical analyses were performed to evaluate the factors

that might influence the bacterial community. The chemical

analyses were done at the Central Analytical Instruments

research Laboratory, Louisiana State University (Baton Rouge,

LA). Metals, anions and total phosphorous were analyzed by

Corresponding author: Mohammed Al-Jawasim, Department of Environmental Science/ University of Al-Qadisiyah, Al-Dewaniya,

8014, Iraq; Tel: 009647832672007; E-mail: mohammedaljawasim@qu.edu.iq

259

Journal of Environmental Treatment Techniques

2021, Volume 9, Issue 1, Pages: 259-263

EPA methods 200.7, 300.0 and 365.3, respectively (Table 1).

Table 1. Chemical characteristics of the salt marsh sediment

addressing the factors that might affect the bacterial

community.

incubated aerobically at 30 °C. The microcosms were sampled

after 60 days of incubation. By using the PowerSoil DNA

Isolation Kit (MoBio Laboratories, Carlsbad, CA), total DNA

was extracted from 0.3 gm of sediments and stored at –20 °C

prior to analysis.

Factor

Value

ND*

0.1

.4 Polymerase chain reaction (PCR)

Nested PCR was implemented to amplify the total bacterial

Aluminum (mg/kg)

Antimony (mg/kg)

Arsenic (mg/kg)

Barium (mg/kg)

Beryllium (mg/kg)

Boron (mg/kg)

Cadmium (mg/kg)

Calcium (mg/kg)

Carbon (%)

16S rRNA gene. The primers 27F and 1522R were used in the

first round of the reaction. The final volume of the PCR mixture

was 50 μL containing 10 pmol of 27F and 1522R primers, 1 μL

of template DNA, 0.25 mM of dNTP, 5 μL of 10x Green Taq

PCR buffer, and 1 U of Green Taq DNA polymerase

12.7

0.7

28.8

0.9

(

GenScript, Piscataway, NJ). PCR was performed with a DNA

thermal cycler (GeneAmp PCR System 2700, Applied

Biosystems, Foster City, CA) at an initial temperature of 94 °C

for 5 minutes, followed by 30 cycles of 94 °C for 20 seconds,

1058.4

7.202

7947.47

17.5

55 °C for 45 seconds, and 72 °C for 45 seconds. A final

Chloride (mg/L)

Chromium (mg/kg)

Cobalt (mg/kg)

Copper (mg/kg)

Fluoride (mg/L)

Iron (mg/kg)

elongation step was carried out at 72 °C for 7 minutes. The

primers 341F and 534R were used in the second round of the

reaction to amplify the V3 region of the 16S rRNA gene [15].

About 1 μL of the PCR products of the first round were used as

a template for the second-PCR-round. PCR constituents and

conditions were the same as described above. The resulting

PCR products were confirmed by an agarose gel

electrophoresis.

117.7

3.97

19913.5

37.2

5563

123.6

Lead (mg/kg)

Magnesium (mg/kg)

Manganese (mg/kg)

Molybdenum (mg/kg)

Nickel (mg/kg)

Nitrate (mg/L)

Nitrite (mg/L)

2.5 Denaturing gradient gel electrophoresis (DGGE)

PCR products of the second-round were separated on an 8%

polyacrylamide gel with a 40-60% denaturing gradient of urea

in 1.0x TAE buffer by a Bio-Rad DCodeTM Universal

Mutation Detection System (Bio-Rad Laboratories, Hercules,

CA). Astacking gel (a non-denaturing polyacrylamide gel) was

prepared to make sample-loading wells on top of the

denaturing-gradient gel. Forty five μL of PCR products were

loaded into the wells. The electrophoresis process was

conducted at 60 °C at 40 V for 15 hours. After electrophoresis,

the gels were stained with ethidium bromide for 15 minutes and

photographed on a UV transilluminator (Fisher Scientific,

Pittsburgh, PA).

15.3

11.38

21.74

0.433

7.06

0.03

605

Nitrogen (%)

Phosphate (mg/L)

Phosphorus (mg/kg)

Potassium (mg/kg)

Selenium (mg/kg)

Silicon (mg/kg)

Sodium (mg/kg)

Sulfate (mg/L)

Sulfur (mg/kg)

Thallium (mg/kg)

Tin (mg/kg)

2364.8

.6 DNA sequencing

Ten DGGE bands were excised from the gel and incubated

776.8

808

separately overnight at 4°C with 50 μL of distilled water to

allow the DNAs to be released into the water. PCR was

performed to re-amplify the eluted DNA. PCR constituents and

conditions were the same as described in the first-round PCR

except that the reaction was carried out for 35 cycles. The purity

and position of the re-amplified DNAs were verified by

conducting the DGGE analysis. If necessary, the DGGE bands

were re-excised and the PCR-DGGE process was repeated until

all the samples showed a single DGGE band. The resulting

PCR products were purified with the MEGAquickspin Total Kit

109.56

5304.7

0.4

Vanadium (mg/kg)

Yttrium (mg/kg)

Zinc (mg/kg)

36.7

(

iNtRON Biotechnology Inc., Korea) for DNAsequencing. The

84.5

purified DNAs were outsourced to the Genewiz Inc. (Genewiz

Inc., South Plainfield, NJ), and each sample was sequenced

separately with forward and reverse primers.

ND: not detected

.3 Microcosms preparation and DNA extraction

The crude oil Western Texas Intermediate (WTI) was

.7 Data analysis

The DGGE image was analyzed by PyElph software

purchased from Texas Raw Crude (Midland TX). The

dispersant Corexit 9500A was provided by the Nalco Energy

Services (Sugar Land TX). Four sets of microcosms, (1)

untreated control, (2) treated with 0.2% (v/w) Corexit 9500A,

(

version 1.4) to examine DGGE bands profiles and to construct

a phylogenetic tree using the unweighted pair group method

with arithmetic mean (UPGMA) algorithm. The DNA

sequences were analyzed using the Chromas Lite (version

(

3) treated with 2% (v/w) WTI, and (4) treated with 0.2%

Corexit 9500A and 2% WTI were prepared in triplicates. One

gram of sediment was aseptically transferred into sterile 2 mL

tubes, sealed with a Teflon-coated cap. Corexit 9500A and

crude oil were added by a micropipette. The microcosms were

.1.1) to assess their quality. In order to confirm queries

identity, the basic local alignment search tool algorithim

BLAST) was used to search homologus sequences in the

(

260

Journal of Environmental Treatment Techniques

2021, Volume 9, Issue 1, Pages: 259-263

GenBank DNA libraries.

Hydrocarboniphaga effusa strain AP103 , Parvibaculum

lavamentivorans strain DS-1

and Alicyclobacillus

ferrooxydans isolate YE3-D4-31i-CH, respectively (table 2).

Hydrocarboniphaga effusa strain AP103 is a hydrocarbon

Results and Discussion

.1 Corexit 9500A and crude oil effects on the bacterial

degrading bacterium, and it has been isolated from crude oil

contaminated environments. This strain degrades particularly

n-alkanes forms of hydrocarbons, and the genomic analysis of

this strain has confirmed presence two genes encoding alkane

omega monooxygenase enzymes (Alk-like enzymes) involving

in alkanes degradation [20]. Parvibaculum lavamentivorans

community structure

The structure of the bacterial community in the salt marsh

sediments was significantly shifted after 60 days exposure to

Corexit 9500A, crude oil, and Corexit 9500A plus crude oil.

The DGGE band patterns, numbers, and intensities in the

treated microcosms were shifted (figure 1A). The bacterial

diversities in the treated microcosms were reduced, and the

abundance of some bacterial species was increased, which was

represented by the intense bands in each treatment. PyElph

analysis showed that the control and crude oil treatments were

phylogenetically close and occupied the first cluster of the tree.

The second cluster included Corexit 9500Aand Corexit 9500A

plus crude oil treatments (Figure 1B).

strain DS-1 has an ability to completely degrade linear

alkylbenzenesulfonate (LAS) surfactants [21], and it is

considered a typical member of many heterotrophic LAS-

degrading bacteria [22].

.2 Phylogenetic analysis of the main DGGE bands

The main DGGE bands in Corexit 9500A treatment were

B1, B2, and B3 (figure 1A). DNA sequence analysis of these

bands suggested that they were phylogenetically close to

Pandoraea thiooxydans strain ATSB16 , Janthinobacterium

sp. T3-QB-2044, and Hyphomicrobium nitrativorans strain

NL23 , respectively (Table 2). Pandoraea thiooxydans strain

ATSB16T,

a facultatively chemolithoautotrophic, sulfur-

oxidizing bacterium, was isolated from a rhizosphere soil of the

sesame plant (Sesamum indicum L.) [16]. Pandoraea

thiooxydans strains of environmental sources are involved in

degradation of many environmental pollutants [17]. The strain

ATSB16 can grow chemolithoautotrophically with sulfur,

sulfite, thiosulfate, and tetrathionate. Furthermore, this strain is

capable of reducing nitrate and hydrolyzing Tween 80 for

growth [16]. The bacterial genus Janthinobacterium includes

several

hydrocarbon-degrading

strains,

such

Janthinobacterium sp. J3 and Janthinobacterium sp. J4.

Janthinobacterium sp. J3 possesses CAR-catabolic genes that

are capable of metabolizing carbazole, an N-hetedrocyclic

aromatic compound has been extracted from crude oil, shale

oil, and creosote [18]. Hyphomicrobium nitrativorans strain

NL23 was isolated from a biofilm of a methanol-fed

denitrification system treating seawater, Canada [19]. The

genome analysis of this strain has identified a number of ORFs

encoding enzymes that are involved in nitrite, nitrate, nitric

oxide, and nitrous oxide reduction. Corexit 9500A's

hydrocarbons and Tween 80, as well as the high concentrations

of nitrate, nitrite, sulfur, and sulfate, might have enhanced the

Figure 1: Bacterial community shift after 60 days of exposure to

Corexit 9500A, crude oil, and Corexit 9500Aplus crude oil. (A) DGGE

profiles of bacterial 16s rRNA gene in sediment microcosms treated

with 0.2% of Corexit 9500A, 2% of crude oil, and 0.2% of Corexit

500A plus 2% of crude oil. (B) Unweighted Pair Group Method with

population

species

Pandoraea

thiooxydans,

Arithmetic Mean (UPGMA) dendrogram of DGGE profiles. The values

on the horizontal lines stand for genetic distances among treatments in

percentages. M: marker; numbers 1, 2, and 3 represent individual

triplicate

Janthinobacterium sp., and Hyphomicrobium nitrativorans to

thrive in these contaminated conditions and dominate the

bacterial community. The DGGE bands B4, B5, and B6 were

the major bands in the crude oil treatment. DNA sequence

analysis of these bands revealed that they were homologous to

Table 2: Phylogenetic affiliation between the isolated DGGE bands and their close relative organisms with the GenBank accession

numbers and percentages identity

Percent

Band

Close relatives in GenBank databases

GenBank Accession no.

identity

99.37

96.42

90.43

86.71

91.77

85.71

84.28

93.08

98.78

93.71

B10

Pandoraea thiooxydans strain ATSB16^T

Janthinobacterium sp. T3-QB-2044

Hyphomicrobium nitrativorans strain NL23

Hydrocarboniphaga effusa strain AP103

Parvibaculum lavamentivorans strain DS-1

Alicyclobacillus ferrooxydans isolate YE3-D4-31i-CH

Janthinobacterium sp. A1-13

Parvibaculum lavamentivorans strain DS-1

Dyella sp. sk100104

NR_116008

KJ922698

NR_121713

NR_029102

NR_074262

FN870342

AB252072

NR_074262

GU552467

261

Journal of Environmental Treatment Techniques

2021, Volume 9, Issue 1, Pages: 259-263

The genus Parvibaculum includes several hydrocarbon-

degrading species, which have been isolated from hydrocarbon

contaminated environments [23, 24]. Crude oil addition and

biosurfactants produced by bacterial degradation of

hydrocarbons might have enhanced this bacterial strain to

dominate the bacterial community in crude oil treated

microcosms. Alicyclobacillus ferrooxydans has the ability to

metabolize various carbon forms as sources for growth and

energy. This species can also grow by oxidation of ferrous iron,

sulfides, and elemental sulfur [25]. Chemical analysis showed

that the salt marsh sediment sample has a high concentration of

iron, sulfate, and sulfur (Table 1).

The major DGGE bands in Corexit 9500A plus crude oil

treatment were B7, B8, B9, and B10 (table 2). DNA sequence

analysis revealed that B7 was phylogenetically homologous to

Janthinobacterium sp. A1-13. Janthinobacterium sp. A1-13,

an acid tolerant bacterium, was isolated from peat soil in

Indonesia [26]. This bacterium inhabits heavily contaminated

industrial wastes [27], and it is considered one of the most

Competing interest

The author declares that there is no conflict of interest that

would prejudice the impartiality of this scientific work.

References

Prince R, Atlas RM. Bioremediation of marine oil spills.

Bioremediation: Applied microbial solutions for real‐world

environmental cleanup. Oil & Gas Science and Technology. 2003

Apr 29:269-92.

2. Brakstad OG, Nordtug T, Throne-Holst M. Biodegradation of

dispersed Macondo oil in seawater at low temperature and different

oil droplet sizes. Marine Pollution Bulletin. 2015 Apr 15;93(1-

):144-52.

Singer MM, George S, Lee I, Jacobson S, Weetman LL, Blondina

G, Tjeerdema RS, Aurand D, Sowby ML. Effects of dispersant

treatment on the acute aquatic toxicity of petroleum hydrocarbons.

Archives of Environmental Contamination and Toxicology. 1998

Feb 1;34(2):177-87.

4. Zahed MA, Aziz HA, Isa MH, Mohajeri L. Effect of initial oil

concentration and dispersant on crude oil biodegradation in

contaminated seawater. Bulletin of Environmental Contamination

and Toxicology. 2010 Apr 1;84(4):438-42.

5. Haritash AK, Kaushik CP. Biodegradation aspects of polycyclic

aromatic hydrocarbons (PAHs): a review. Journal of Hazardous

Materials. 2009 Sep 30;169(1-3):1-5.

important N O-producing bacteria in such environments [26].

The bands B8 and B9 were homologous to Parvibaculum

lavamentivorans strain DS 1 . Parvibaculum lavamentivorans

strain DS-1 has the ability to completely degrade linear

alkylbenzenesulfonate (LAS), a major laundry surfactant [21].

Corexit 9500A surfactants might have enriched this strain

under these conditions. The band B10 was homologous to

Dyella sp. sk100104. This strain was isolated from a

contaminated forest soil with a mixture of xenobiotics,

Alabresm A, Chen YP, Decho AW, Lead J. A novel method for

the synergistic remediation of oil-water mixtures using

nanoparticles and oil-degrading bacteria. Science of the Total

Environment. 2018 Jul 15;630:1292-7.

Ramachandran SD, Hodson PV, Khan CW, Lee K. Oil dispersant

increases PAH uptake by fish exposed to crude oil. Ecotoxicology

and Environmental Safety. 2004 Nov 1;59(3):300-8.

Fiocco RJ, Lewis A. Oil spill dispersants. Pure and Applied

Chemistry. 1999 Jan 1;71(1):27-42.

Atlas RM, Hazen TC. Oil biodegradation and bioremediation: a

tale of the two worst spills in US history. Environmental Science

and Technology. 2011;45:6709-15.

including 1-amino-2-propanol (APOL),

methyl-2-

pyrrolidinone (MP), 1- dioxide (THT), diethylene glycol

monoethyl ether (DGMEE), diethylene glycol monomethyl

ether (DGMME), tetraethylene glycol (TEG), and

tetramethylammonium hydroxide (TMAH), and this bacterium

ability to degrade these contaminants has been reported [28].

The majority of these compounds are glycol-based solvents,

which are similar to Corexit 9500A constituents.

10. Prince RC, Butler JD. A protocol for assessing the effectiveness of

oil spill dispersants in stimulating the biodegradation of oil.

Environmental Science and Pollution Research. 2014 Aug

;21(16):9506-10.

Conclusion

1. Techtmann SM, Zhuang M, Campo P, Holder E, Elk M, Hazen TC,

Conmy R, Santo Domingo JW. Corexit 9500 enhances oil

biodegradation and changes active bacterial community structure

of oil-enriched microcosms. Applied and Environmental

Microbiology. 2017 May 15;83(10). e03462-16.

2. Swannell RP, Daniel F, Croft BC, Engelhardt MA, Wilson S,

Mitchell DJ, Lunel T. Influence of physical and chemical

dispersion on the biodegradation of oil under simulated marine

conditions. In Arctic and marine oil spill program technical

seminar. 1997 Jun (Vol. 1, pp. 617-642). Ministry of supply and

Services, Canada.

13. Bælum J, Borglin S, Chakraborty R, Fortney JL, Lamendella R,

Mason OU, Auer M, Zemla M, Bill M, Conrad ME, Malfatti SA.

Deep‐sea bacteria enriched by oil and dispersant from the

Deepwater Horizon spill. Environmental Microbiology. 2012

Sep;14(9):2405-16.

4. Al-Jawasim M, Yu K, Park JW. Synergistic effect of crude oil plus

dispersant on bacterial community in a Louisiana salt marsh

sediment. FEMS Microbiology Letters. 2015 Sep 1;362(17).

The structure of the bacterial community in the salt marsh

sediments was significantly shifted in response to

Corexit9500A plus crude oil treatment, and it was different

from those either Corexit 9500Aor crude oil treatment. Corexit

500A addition to crude oil showed combined effects on the

bacterial community and enhanced the biodegradation rate by

way of increasing the diversity and richness of hydrocarbons

degrading species. Further studies are required to determine the

long-term combined effects of Corexit 9500Aplus crude oil on

the environment to evaluate the environmental impacts of

dispersants application during oil spills.

Acknowledgement

I am grateful for the Higher Committee for Education

Development in Iraq (HCED) and Troy University, Troy, AL.

USA/ the Faculty Development Research grants, for funding

this research.

15. Muyzer G, De Waal EC, Uitterlinden AG. Profiling of complex

microbial populations by denaturing gradient gel electrophoresis

analysis of polymerase chain reaction-amplified genes coding for

Ethical issue

Author is aware of, and comply with, best practice in

publication ethics specifically with regard to authorship

6S rRNA. Applied and Environmental Microbiology. 1993 Mar

;59(3):695-700.

6. Anandham R, Indiragandhi P, Kwon SW, Sa TM, Jeon CO, Kim

YK, Jee HJ. Pandoraea thiooxydans sp. nov., a facultatively

chemolithotrophic, thiosulfate-oxidizing bacterium isolated from

rhizosphere soils of sesame (Sesamum indicum L.). International

Journal of Systematic and Evolutionary Microbiology. 2010 Jan

(

avoidance of guest authorship), dual submission, manipulation

of figures, competing interests and compliance with policies on

research ethics. Authors adhere to publication requirements that

submitted work is original and has not been published

elsewhere in any language.

;60(1):21-6.

7. Jiang XW, Liu H, Xu Y, Wang SJ, Leak DJ, Zhou NY. Genetic

and biochemical analyses of chlorobenzene degradation gene

262

Journal of Environmental Treatment Techniques

2021, Volume 9, Issue 1, Pages: 259-263

clusters in Pandoraea sp. strain MCB032. Archives of

Microbiology. 2009 Jun 1;191(6):485-92.

8. Inoue K, Widada J, Nakai S, Endoh T, Urata M, Ashikawa Y,

Shintani M, Saiki Y, Yoshida T, Habe H, Omori T. Divergent

structures of carbazole degradative car operons isolated from

Gram-negative bacteria. Bioscience, Biotechnology, and

Biochemistry. 2004 Jan 1;68(7):1467-80.

9. Martineau C, Villeneuve C, Mauffrey F, Villemur R. Complete

genome sequence of Hyphomicrobium nitrativorans strain NL23 ,

a denitrifying bacterium isolated from biofilm of a methanol-fed

denitrification system treating seawater at the Montreal Biodome.

Genome Announcements. 2014 Feb 27;2(1). 2:e01165-13.

0. Chang HK, Zylstra GJ, Chae JC. Genome Sequence of n-Alkane-

Degrading Hydrocarboniphaga effusa Strain AP103 (ATCC

BAA-332 ). Journal of Bacteriology. 2012; 194:5120-25.

1. Schleheck D, Knepper TP, Eichhorn P, Cook AM. Parvibaculum

lavamentivorans DS-1^Tdegrades centrally substituted congeners

of commercial linear alkylbenzenesulfonate to sulfophenyl

carboxylates and sulfophenyl dicarboxylates. Applied and

Environmental Microbiology. 2007 Aug 1;73(15):4725-32.

2. Dong W, Eichhorn P, Radajewski S, Schleheck D, Denger K,

Knepper TP, Murrell JC, Cook AM. Parvibaculum

lavamentivorans

converts

linear

alkylbenzenesulphonate

surfactant to sulphophenylcarboxylates, α, β‐unsaturated

sulphophenylcarboxylates and sulphophenyldicarboxylates, which

are degraded in communities. Journal of Applied Microbiology.

004 Mar;96(3):630-40.

3. Alonso-Gutiérrez J, Figueras A, Albaigés J, Jiménez N, Vinas M,

Solanas AM, Novoa B. Bacterial communities from shoreline

environments (Costa da Morte, Northwestern Spain) affected by

the Prestige oil spill. Applied and Environmental Microbiology.

009 Jun 1;75(11):3407-18.

4. Wang L, Wang W, Lai Q, Shao Z. Gene diversity of CYP153A and

AlkB alkane hydroxylases in oil‐degrading bacteria isolated from

the Atlantic Ocean. Environmental Microbiology. 2010

May;12(5):1230-42.

5. Jiang CY, Liu Y, Liu YY, You XY, Guo X, Liu SJ.

Alicyclobacillus ferrooxydans sp. nov.,

a ferrous-oxidizing

bacterium from solfataric soil. International Journal of Systematic

and Evolutionary Microbiology. 2008 Dec 1;58(12):2898-903.

6. Hashidoko Y, Takakai F, Toma Y, Darung U, Melling L, Tahara

S, Hatano R. Emergence and behaviors of acid-tolerant

Janthinobacterium sp. that evolves N2O from deforested tropical

peatland. Soil Biology and Biochemistry. 2008 Jan 1;40(1):116-

7. Maukonen J, Saarela M. Microbial communities in industrial

environment. Current Opinion in Microbiology. 2009 Jun

;12(3):238-43.

8. Jeon BY, Park DH. Isolation of xenobiotic-degrading bacteria and

analysis of bacterial community variation in soil microcosm

contaminated with xenobiotics. Journal of the Korean Society for

Environmental Analysis. 2010;13(2):85-91.

263