DOCSLIB.ORG

Laboratory, Field, and Modeling Studies of Bioaugmentation Of

Total Page：16

File Type：pdf, Size：1020Kb

Download full-text PDF Read full-text
Laboratory, Field, and Modeling Studies of Bioaugmentation Of Advances in Water Resources 30 (2007) 1528–1546 www.elsevier.com/locate/advwatres Laboratory, field, and modeling studies of bioaugmentation of butane-utilizing microorganisms for the in situ cometabolic treatment of 1,1-dichloroethene, 1,1-dichloroethane, and 1,1,1-trichloroethane Lewis Semprini a,*, Mark E. Dolan a, Maureen A. Mathias a, Gary D. Hopkins b, Perry L. McCarty b a Department of Civil, Construction and Environmental Engineering, Oregon State University, Apperson Hall 202, Corvallis, OR 97331-2302, United States b Department of Civil and Environmental Engineering, Stanford University, United States Received 29 July 2005; received in revised form 10 April 2006; accepted 5 May 2006 Available online 18 September 2006 Abstract A series of laboratory, field, and modeling studies were performed evaluating the potential for in situ aerobic cometabolism of chlo- rinated aliphatic hydrocarbon (CAH) mixtures, including 1,1,1-trichloroethane (1,1,1-TCA), 1,1-dichloroethane (1,1-DCA) and 1,1- dichloroethene (1,1-DCE) by bioaugmented microorganisms that grew on butane. A butane-grown bioaugmentation culture, primarily comprised of a Rhodococcus sp., was developed that effectively transformed mixtures of the three CAHs, under subsurface nutrient con- ditions. Microcosm experiments and modeling studies showed rapid transformation of 1,1-DCE with high transformation product tox- icity and weak inhibition by butane, while 1,1,1-TCA was much more slowly transformed and strongly inhibited by butane. Field studies were conducted in the saturated zone at the Moffett Field In-Situ Test Facility in California. In the bioaugmented test leg, 1,1-DCE was most effectively transformed, followed by 1,1-DCA, and 1,1,1-TCA, consistent with the results from the laboratory studies. A 1-D reac- tive/transport code simulated the field responses during the early stages of testing (first 20 days), with the following extents of removal achieved at the first monitoring well; 1,1-DCE (97%), 1,1-DCA (77%), and 1,1,1-TCA (36%), with little or no CAH transformation observed beyond the first monitoring well. As time proceeded, decreased performance was observed. The modeling analysis indicated that this loss of performance may have been associated with 1,1-DCE transformation toxicity combined with the limited addition of butane as a growth substrate with longer pulse cycles. When shorter pulse cycles were reinitiated after 40 days of operation, 1,1-DCE transformation was restored and the following transformation extents were achieved; 1,1-DCE (94%), 1,1-DCA (8%), and 1,1,1- TCA (0%), with some CAH transformation occurring past the first monitoring well. Modeling analysis of this period indicated that the bioaugmented culture was likely not the dominant butane-utilizing microorganism present. This was consistent with observations in the indigenous leg during this period that showed effective butane utilization and the following extents of transformation: 1,1- DCE (86 %), 1,1-DCA (5%), and 1,1,1-TCA (0%). The combination of lab and field scale studies and supporting modeling provide a means of evaluating the performance of bioaugmentation and the cometabolic treatment of CAH mixtures. Ó 2006 Elsevier Ltd. All rights reserved. Keywords: Cometabolism; Modeling; Field tests; Bioaugmentation; Butane; 1,1-Dichloroethene, 1,1-Dichloroethane; 1,1,1-Trichloroethane; Inhibition; Transformation toxicity; CAH mixtures 1. Introduction In situ aerobic cometabolism has been shown to be a method for reducing groundwater contamination with * Corresponding author. Fax: +1 541 7373099. chlorinated aliphatic hydrocarbons (CAHs) [26,12,21]. E-mail address: [email protected] (L. Semprini). Cometabolic transformation results from non-specific 0309-1708/$ - see front matter Ó 2006 Elsevier Ltd. All rights reserved. doi:10.1016/j.advwatres.2006.05.017 L. Semprini et al. / Advances in Water Resources 30 (2007) 1528–1546 1529 Nomenclature Parameter Definition X cell concentration on a pore volume basis (mg/L) KIc,DCE,BUT competitive inhibition constant of 1,1-DCE X0 initial cell concentration on a pore volume basis on butane (mg/L) (mg/L) KIc,DCA,BUT competitive inhibition constant of 1,1- Y cell yield (mg cells/mg butane) DCA on butane (mg/L) b cell decay coefficient (dÀ1) KIc,TCA,BUT competitive inhibition constant of 1,1,1- Fa stoichiometric ratio of oxygen to butane for bio- TCA on butane (mg/L) mass synthesis (mg O2/mg butane) KIc,DCE,DCA competitive inhibition constant of 1,1-DCE VL liquid volume (L) on 1,1-DCA (mg/L) VG gas volume (L) À1 KIc,DCE,TCA competitive inhibition constant of 1,1-DCE Kla overall gas/liquid mass transfer coefficient (d ) on 1,1,1-TCA (mg/L) km DCE maximum transformation rate of 1,1-DCE (mg KIc,DCA,DCE competitive inhibition constant of 1,1- 1,1-DCE/mg cells-d) DCA on 1,1-DCE (mg/L) km DCA maximum transformation rate of 1,1-DCA (mg KIc,DCA,TCA competitive inhibition constant of 1,1- 1,1-DCA/mg cells-d) DCA on 1,1,1-TCA (mg/L) km TCA maximum transformation rate of 1,1,1-TCA KIc,TCA,DCE competitive inhibition constant of 1,1,1- (mg 1,1,1-TCA/mg cells-d) TCA on 1,1-DCE (mg/L) km BUT maximum utilization rate of butane (mg butane/ KIc,TCA,DCA competitive inhibition constant of 1,1,1- mg cell-d) TCA on 1,1-DCA (mg/L) C aqueous substrate concentration (mg/L) KIc,BUT,DCE competitive inhibition constant of butane Ks DCE half-saturation constant of 1,1-DCE (mg/L) on 1,1-DCE (mg/L) Ks DCA half-saturation constant of 1,1-DCA (mg/L) KIc,BUT,DCA competitive inhibition constant of butane Ks TCA half-saturation constant of 1,1,1-TCA (mg/L) on 1,1-DCA (mg/L) Ks BUT half-saturation constant of butane (mg/L) KIc,BUT,TCA competitive inhibition constant of butane Tc DCE transformation capacity of 1,1-DCE (mg 1,1- on 1,1,1-TCA (mg/L) DCE/mg cells) KIu,BUT,DCE non-competitive inhibition constant of bu- Tc DCA transformation capacity of 1,1-DCA (mg 1,1- tane on 1,1-DCE (mg/L) DCA/mg cells) KIu,BUT,DCA non-competitive inhibition constant of bu- Tc TCA transformation capacity of 1,1,1-TCA (mg tane on 1,1-DCA (mg/L) 1,1,1-TCA/mg cells) * KIu,BUT,TCA non-competitive inhibition constant of bu- C sorbed phase substrate concentration (mg sub- tane on 1,1,1-TCA (mg/L) strate/kg soil) 2 Hcc,DCE dimensionless Henrys constant for 1,1-DCE Dh hydrodynamic dispersion coefficient (m /d) À1 Hcc,DCA dimensionless Henrys constant for 1,1-DCA Fk mass transfer rate coefficient for sorption (d ) Hcc,TCA dimensionless Henrys constant for 1,1,1-TCA v average linear groundwater velocity (m/d) Hcc,BUT dimensionless Henrys constant for butane Kd partition coefficient for sorption (L/kg) fd fraction of cells that are biodegradable (mg/mg) U porosity dc cell decay oxygen demand (mg O2/mg cell) qb bulk density of the aquifer solids (kg/L) enzymes fortuitously catalyzing these reactions. Because Microorganisms that grow on butane have the ability to these reactions do not provide energy or carbon, a primary cometabolize a broad range of CAHs [9,8,15,14]. Microor- growth substrate must be supplied to stimulate the neces- ganisms stimulated on butane are capable of transform- sary population of cometabolizing microorganisms. In oxi- ing 1,1-dichloroethene (1,1-DCE), 1,1-dichloroethane dative cometabolism, the enzymes use the primary growth (1,1-DCA), and 1,1,1-trichloroethane (1,1,1-TCA) [17]. substrate as an electron donor and oxygen as an electron Kim et al. [16,17] performed detailed kinetic and inhibition acceptor. studies on the cometabolic transformation of these three The performance of cultures capable of cometabolic oxi- CAHs with a butane-grown enrichment culture. 1,1-DCE dative dechlorination has been studied for a variety of con- was observed to have the fastest transformation kinetics, taminants and primary growth substrates as reviewed by followed by 1,1-DCA, and 1,1,1-TCA. Inhibition models Arp et al. [4] and Alvarez-Cohen and Speitel [2]. Examples were also determined for butane inhibition on CAH trans- of monooxygenase-inducing substrates include methane, formation, CAH inhibition on butane utilization, and propane, ammonia, toluene, and phenol [9,8,3,5]. CAH inhibition on each others’ transformation. These 1530 L. Semprini et al. / Advances in Water Resources 30 (2007) 1528–1546 inhibitions play an important role in application of comet- substrate, PR1301 did not maintain TCE degradative ability abolic transformations and are incorporated into our for long periods. model development. A microcosm study with the butane-enrichment culture Glotz et al. [7] reviewed models for cometabolism, of Kim et al. [16] was conducted by Jitnuyanont et al. [13] including transport models and the use of models in the to study the transformation of 1,1,1-TCA in bioaugmented design of remediation systems. The modeling of cometab- and non-augmented microcosms. The augmented micro- olism both in batch systems and transport codes involves cosms required less time to start utilization of butane than the incorporation of processes including microbial growth non-augmented microcosms and initially were more effec- and decay, substrate utilization as an electron donor, oxy- tive in transforming 1,1,1-TCA, but their transformation gen utilization as an electron acceptor, and the transfor- ability decreased with prolonged incubation. mation of the CAHs of interest. The multi-species The objectives of our study were to: (1) develop a culture reactive transport models must also include key cometa- for bioaugmentation from a parent culture that had been bolic processes including the kinetics of different inhibi- kinetically well characterized by Kim et al.
Load more

Recommended publications
  • Bioaugmentation: an Emerging Strategy of Industrial Wastewater Treatment for Reuse and Discharge
    International Journal of Environmental Research and Public Health Review Bioaugmentation: An Emerging Strategy of Industrial Wastewater Treatment for Reuse and Discharge Alexis Nzila 1,*, Shaikh Abdur Razzak 2 and Jesse Zhu 3 1 Department of Life Sciences, King Fahd University of Petroleum and Minerals (KFUPM), P.O. Box 468, Dhahran 31261, Saudi Arabia 2 Department of Chemical Engineering, King Fahd University of Petroleum and Minerals (KFUPM), Dhahran 31261, Saudi Arabia; [email protected] 3 Department of Chemical and Biochemical Engineering, University of Western Ontario, London, ON N6A 5B9, Canada; [email protected] * Correspondence: [email protected]; Tel.: +966-13-860-7716; Fax: +966-13-860-4277 Academic Editors: Rao Bhamidiammarri and Kiran Tota-Maharaj Received: 12 May 2016; Accepted: 9 July 2016; Published: 25 August 2016 Abstract: A promising long-term and sustainable solution to the growing scarcity of water worldwide is to recycle and reuse wastewater. In wastewater treatment plants, the biodegradation of contaminants or pollutants by harnessing microorganisms present in activated sludge is one of the most important strategies to remove organic contaminants from wastewater. However, this approach has limitations because many pollutants are not efficiently eliminated. To counterbalance the limitations, bioaugmentation has been developed and consists of adding specific and efficient pollutant-biodegrading microorganisms into a microbial community in an effort to enhance the ability of this microbial community to biodegrade contaminants. This approach has been tested for wastewater cleaning with encouraging results, but failure has also been reported, especially during scale-up. In this review, work on the bioaugmentation in the context of removal of important pollutants from industrial wastewater is summarized, with an emphasis on recalcitrant compounds, and strategies that can be used to improve the efficiency of bioaugmentation are also discussed.
    [Show full text]
  • Bioaugmentation of Chlorinated Solvents
    BIOAUGMENTATION FOR REMEDIATION OF CHLORINATED SOLVENTS: TECHNOLOGY DEVELOPMENT, STATUS, AND RESEARCH NEEDS October 2005 GeoSyntec Consultants TABLE OF CONTENTS LIST OF TABLES ...........................................................................................................................................III LIST OF FIGURES .........................................................................................................................................III ACRONYMNS AND ABBREVIATIONS........................................................................................................V FOREWORD...................................................................................................................................................VII EXECUTIVE SUMMARY ............................................................................................................................... IX 1. INTRODUCTION ..........................................................................................................................................1 2. EARLY DEVELOPMENT OF BIOAUGMENTATION.............................................................................5 3. RECENT PROGRESS IN CHLORINATED SOLVENT BIOREMEDIATION .....................................13 4. DEHALORESPIRATION: THE KEY PROCESS UNDERLYING CURRENT BIOAUGMENTATION PRACTICES..............................................................................................................................................................19 4.1 THE UBIQUITY CONCEPT REVISITED
    [Show full text]
  • Biological Methods
    Biological Methods Jerry Walsh, Jenna Bishop, Quinn Albertson, Shane Galloway, Carlos Rivera, Tom Devenney, Jeff Green Physical Mechanisms In Situ Methods Permeable Reactive Barriers Biostimulation Bioaugmentation Phytoremediation Permeable Reactive Barriers (Biobarriers) • Semi-permeable reactive media in flow path • Chemically or biologically-mediated reactions transform contaminants into non-toxic or immobile products • Hydrocarbons need to be oxidized • Chlorinated solvents and nitrate need to be reduced • Microorganisms help mediate redox reactions to gain energy and materials for synthesis Reactive Media Reactive Medium Removal Mechanism Contaminants Removed Organic Material Microbial sulfate reduction Acid mine drainage and precipitation Organic Material Microbial nitrate reduction Nitrate Oxygen/Nitrate-Releasing Microbial degradation BTEX Compounds Resting-State Microbial cometabolism Chlorinated aliphatics Microorganisms Oxidative Biodegradation • To respire electrons removed from contaminants, need electron acceptors Aerobic: • Aerobic methods Molecular Oxygen Anaerobic: • Anaerobic methods Nutrients (nitrate, sulfates, CO2, ferric iron, metal oxides, etc) • Aerobic methods are generally preferred to provide more energy to the microbes • Biochemical oxygen demands (BOD’s) often exceed available oxygen, so adding oxygen to the system can stimulate oxidative biodegradation Reductive Biodegradation • Electron donors are required, which anaerobic environments more abundantly produce • Organic matter is a well-suited electron donor for this process • This method works well for TCE, hexavalent chromium, sulfate, and nitrate contamination • Heterotrophic denitrification to remove nitrate Biostimulation • Modification of environment to stimulate existing bacteria capable of bioremediation. • Only works if correct bacteria are present. • Often done through use of phosphorous, nitrogen, carbon, and oxygen. • Chemicals usually added through injection wells. • EPA approved method. Advantages • Low Costs • Can be tailored to the specific site conditions.
    [Show full text]
  • Selecting Bacteria Candidates for the Bioaugmentation of Activated Sludge to Improve the Aerobic Treatment of Landfill Leachate
    water Article Selecting Bacteria Candidates for the Bioaugmentation of Activated Sludge to Improve the Aerobic Treatment of Landfill Leachate Justyna Michalska *, Artur Pi ´nski , Joanna Zur˙ and Agnieszka Mrozik Institute of Biology, Biotechnology and Environmental Protection, Faculty of Natural Sciences, University of Silesia, Jagiello´nska28, 40-032 Katowice, Poland; [email protected] (A.P.); [email protected] (J.Z.);˙ [email protected] (A.M.) * Correspondence: [email protected] Received: 6 November 2019; Accepted: 27 December 2019; Published: 1 January 2020 Abstract: In this study, a multifaceted approach for selecting the suitable candidates for bioaugmentation of activated sludge (AS) that supports leachate treatment was used. To determine the exploitation of 10 bacterial strains isolated from the various matrices for inoculating the AS contaminated with the Kalina pond leachate (KPL), their degradative potential was analyzed along with their aptitude to synthesize compounds improving remediation of pollutants in wastewater and ability to incorporate into the AS flocs. Based on their capability to degrade aromatic compounds (primarily catechol, phenol, and cresols) at a concentration of 1 mg/mL and survive in 12.5% of the KPL, Pseudomonas putida OR45a and P. putida KB3 can be considered to be the best candidates for bioaugmentation of the AS among all of the bacteria tested. Genomic analyses of these two strains revealed the presence of the genes encoding enzymes related to the metabolism of aromatic compounds. Additionally, both microorganisms exhibited a high hydrophobic propensity (above 50%) and an ability to produce biosurfactants as well as high resistance to ammonium (above 600 µg/mL) and heavy metals (especially chromium).
    [Show full text]
  • Bioremediation of Groundwater: an Overview
    International Journal of Applied Engineering Research ISSN 0973-4562 Volume 13, Number 24 (2018) pp. 16825-16832 © Research India Publications. http://www.ripublication.com Bioremediation of Groundwater: An Overview Shivam Mani Tripathi 1, Shri Ram2 1 ,2 Civil Engineering Department, MMMUT Gorakhpur, India Abstract can be treated on site, thus reducing exposure risks for clean- In past, we have large open area and abundant land resources up personnel, or potentially wider exposure as a result of and groundwater. But after the industrialization the use of transportation accidents. Methodology of this process is not hazardous chemicals increased due to unmanageable technically difficult, considerable experience and knowledge conditions. The chemical disposed on the ground surface & may require implementing this process, by thoroughly many other anthropogenic activities by humans like use of investigating the site and to know required condition to pesticides and oil spillage contaminated the soil and achieve. groundwater. The different type of contaminant by percolation The usual technique of remediation is to plow up through the ground reach to the aquifer and get affected which contaminated soil and take away to the site, or to cover or cap causes serious problem. We spend lot of money and use many the contaminated area. There are some drawbacks. The first technologies to extract and remediate the contamination. In method simply transport the contaminated materials which spite of different methods, bioremediation is a technology create major risks is excavation, handling, and transport of which is cost efficient and effective by using natural microbes hazardous material. It is very difficult to find the new landfill and degrades the contaminants the conditions and different sites for disposal.
    [Show full text]
  • Advances in Anaerobic Benzene Bioremediation: Microbes, Mechanisms, and Biotechnologies
    Advances in Anaerobic Benzene Bioremediation: Microbes, Mechanisms, and Biotechnologies Sandra Dworatzek, Phil Dennis and Jeff Roberts RemTech, Virtual October 15, 2020 Introduction and Acknowledgements • Sandra Dworatzek, Jennifer Webb (SiREM, Guelph, ON) • Elizabeth Edwards, Nancy Bawa, Shen Guo and Courtney Toth (University of Toronto, Toronto, ON) • Kris Bradshaw and Rachel Peters (Federated Co-operatives Ltd., Saskatoon, SK) • Krista Stevenson (Imperial Oil, Sarnia, ON) The Landscape of Hydrocarbon Bioremediation: A Lot Has Changed… Microbial bioremediation is currently the most common technology used to remediate petroleum hydrocarbons Microbial Remediation Phytoremediation Chemical Treatment Contain and Excavate Pump and Treat Other Near Cold Lake, Alberta Adapted from Elekwachi et al., 2014 (J Bioremed Biodeg 5) What Sites are Currently Being Targeted for Hydrocarbon Bioremediation? 4 Shallow Soils and Groundwater 1 2 (aerobic) Offshore Spills Ex situ Bioreactors (mostly aerobic) (mostly aerobic) 3 Tailings Ponds 5 Deeper Groundwater (aerobic and anaerobic) (intrinsically anaerobic) Groundwater Bioremediation Technologies Focusing on Anaerobic Microbial Processes Natural Attenuation Biostimulation Bioaugmentation unsaturated zone aquifer 3- PO4 sugars Plume source - 2- NO3 SO4 VFAs GW flow aquitard Bioaugmentation for anaerobic sites works! Dehalococcoides (Dhc) bioaugmentation is widely accepted to improve reductive dehalogenation of chlorinated ethenes 1 Month Post KB-1® Bioaugmentation Dhc TCE Bioaugmentation for anaerobic
    [Show full text]
  • Microbial Community Changes in Methyl Tert-Butyl Ether (MTBE)- Contaminated Soils
    University of Tennessee, Knoxville TRACE: Tennessee Research and Creative Exchange Masters Theses Graduate School 8-2004 Microbial Community Changes in Methyl tert-Butyl Ether (MTBE)- Contaminated Soils Bo Yang University of Tennessee - Knoxville Follow this and additional works at: https://trace.tennessee.edu/utk_gradthes Part of the Civil and Environmental Engineering Commons Recommended Citation Yang, Bo, "Microbial Community Changes in Methyl tert-Butyl Ether (MTBE)-Contaminated Soils. " Master's Thesis, University of Tennessee, 2004. https://trace.tennessee.edu/utk_gradthes/2223 This Thesis is brought to you for free and open access by the Graduate School at TRACE: Tennessee Research and Creative Exchange. It has been accepted for inclusion in Masters Theses by an authorized administrator of TRACE: Tennessee Research and Creative Exchange. For more information, please contact [email protected]. To the Graduate Council: I am submitting herewith a thesis written by Bo Yang entitled "Microbial Community Changes in Methyl tert-Butyl Ether (MTBE)-Contaminated Soils." I have examined the final electronic copy of this thesis for form and content and recommend that it be accepted in partial fulfillment of the requirements for the degree of Master of Science, with a major in Environmental Engineering. Kung-Hui Chu, Major Professor We have read this thesis and recommend its acceptance: Chris D. Cox, Paul D. Frymier Accepted for the Council: Carolyn R. Hodges Vice Provost and Dean of the Graduate School (Original signatures are on file with official studentecor r ds.) To the Graduate Council: I am submitting herewith a thesis written by Bo Yang entitled “Microbial Community Changes in Methyl tert-Butyl Ether (MTBE)-Contaminated Soils.” I have examined the final electronic copy of this thesis for form and content and recommend that it be accepted in partial fulfillment of the requirements for the degree of Master of Science, with a major in Environmental Engineering.
    [Show full text]
  • Strategies for Remediation of Polycyclic Aromatic Hydrocarbons from Contaminated Soil-An Overview
    Innovare Journal of Critical Reviews Academic Sciences ISSN- 2394-5125 Vol 2, Issue 1, 2015 Review Article STRATEGIES FOR REMEDIATION OF POLYCYCLIC AROMATIC HYDROCARBONS FROM CONTAMINATED SOIL-AN OVERVIEW NILANJANA DAS*, DEVLINA DAS Bioremediation Laboratory, SBST, VIT University, Vellore 632014, Tamil Nadu, India. Email: [email protected] Received: 05 Oct 2014 Revised and Accepted: 23 Dec 2014 ABSTRACT Polycyclic aromatic hydrocarbons (PAHs) are one of the most prevalent contaminants having toxicity, mutagenecity and carcinogenicity. Pollution caused by PAHs is a serious problem throughout the world. To solve the problem, substantial research efforts have been directed worldwide to adopt sustainable technologies for the treatment of PAHs containing soil. PAH compounds are transferred, degraded and sequestered in soils. They are relocated in the environment through volatilization, adsorption, leaching and erosion without alteration in their structure. Degradation causes alteration of PAHs structures from their original form though biological and chemical processes and sequestration occurs when PAHs are removed from bioavailable pools and stored for a long period of time. The conventional techniques for PAH removal involve excavation of contaminated soil and its incineration which are quite expensive and in many cases pollutants are transferred from one phase to another. The commonly employed biological methods for PAHs remediation in soil are landfarming, composting, bioaugmentation, biostimulation, phytoremediation etc. and chemical
    [Show full text]
  • Bioremediation and Phytoremediation Systems for Breaking Down Total
    University of Connecticut OpenCommons@UConn Master's Theses University of Connecticut Graduate School 12-14-2014 Bioremediation and Phytoremediation Systems for Breaking Down Total Petroleum Hydrocarbons (TPH) in Contaminated Sandy Soil Patrick McIntosh University of Connecticut - Storrs, [email protected] Recommended Citation McIntosh, Patrick, "Bioremediation and Phytoremediation Systems for Breaking Down Total Petroleum Hydrocarbons (TPH) in Contaminated Sandy Soil" (2014). Master's Theses. 705. https://opencommons.uconn.edu/gs_theses/705 This work is brought to you for free and open access by the University of Connecticut Graduate School at OpenCommons@UConn. It has been accepted for inclusion in Master's Theses by an authorized administrator of OpenCommons@UConn. For more information, please contact [email protected]. Bioremediation and Phytoremediation Systems for Breaking Down Total Petroleum Hydrocarbons (TPH) in Contaminated Sandy Soil Patrick M. McIntosh, B.S., B.S. University of Connecticut 2008 A Thesis Presented in Partial Fulfillment for the Requirements for the Degree Masters of Science in the Graduate School of the University of Connecticut 2014 APPROVAL PAGE MASTERS OF SCIENCE THESIS Bioremediation and Phytoremediation Systems for Breaking Down Total Petroleum Hydrocarbons (TPH) in Contaminated Sandy Soil Presented by Patrick M. McIntosh B.S., B.S. Major Advisor ____________________________________________ Julia Kuzovkina Associate Advisor _____________________________________________ Karl Guillard Associate Advisor _____________________________________________ Cristian P. Schulthess The University of Connecticut 2014 II ACKNOWLEDGEMENTS I would like to thank the following individuals whose help make all of this possible: • Dr. Julia Kuzovkina, who gave me the opportunity to pursue this application of higher education. Her constant, support, and concern with these projects was greatly appreciated, especially through the tedious editing process I put her through with all of my corrections.
    [Show full text]
  • Bioremediation: a General Outline
    TECHNICAL GUIDANCE DOCUMENT OCTOBER 31, 2017 INDIANA DEPARTMENT OF ENVIRONMENTAL MANAGEMENT Bioremediation: A General Outline Eric J. Holcomb Bruno L. Pigott Governor Commissioner (317) 232-8603 • (800) 451-6027 www.idem.IN.gov 100 N. Senate Ave., Indianapolis, IN 46204 TECHNICAL GUIDANCE DOCUMENT Guidance Created: May 13, 2005 Revised: April 2007, March 2010, July 27, 2016, and October 31, 2017 Notice IDEM Technology Evaluation Group (TEG) completed this general outline for bioremediation based on review of items listed in the “References” section of this document. This evaluation does not approve this technology nor does it verify its effectiveness in conditions not identified here. Mention of trade names or commercial products does not constitute endorsement or recommendation by IDEM for use. Background This document provides a short overview with terms and notes as to applications and general effectiveness of aerobic (oxygen present) and anaerobic (oxygen absent) bioremediation. Bioremediation is a form of remediation resulting from microbial action. Normal soils and aquifers contain a wide range of naturally occurring microbes, which interact in a complex micro-ecosystem (or microcosm). Although concentrated contaminants (NAPL) may kill almost all microbes, some species will feed on and degrade many less concentrated contaminants. Aerobic bioremediation is the most active force in the natural destruction of non-chlorinated contamination, while anaerobic bioremediation is more effective for chlorinated compounds. Bioremediation is sometimes confused with natural attenuation. Natural attenuation is more encompassing and includes the degradation of contaminants through dilution, adsorption, biological activity, and chemical transformation. Applied correctly under proper site conditions, some additives can improve the speed of bioremediation.
    [Show full text]
  • Bioremediation, Biostimulation and Bioaugmention: a Review
    International Journal of Environmental Bioremediation & Biodegradation, 2015, Vol. 3, No. 1, 28-39 Available online at http://pubs.sciepub.com/ijebb/3/1/5 © Science and Education Publishing DOI:10.12691/ijebb-3-1-5 Bioremediation, Biostimulation and Bioaugmention: A Review Godleads Omokhagbor Adams1,*, Prekeyi Tawari Fufeyin1, Samson Eruke Okoro2, Igelenyah Ehinomen1 1Department of Animal and Environmental Biology, University of Benin, Edo State Nigeria 2Department of Biochemistry, University of Port Harcourt, Rivers State Nigeria *Corresponding author: [email protected] Received February 21, 2015; Revised February 28, 2015; Accepted March 05, 2015 Abstract Bioremediation uses microbial metabolism in the presence of optimum environmental conditions and sufficient nutrients to breakdown contaminants notably petroleum hydrocarbons. We reviewed technologies for carrying out bioremediation and observed that biotechnological approaches that are designed to carry out remediation have received a great deal of attention in recent years. Biostimulation (meaning the addition of limiting nutrients to support microbial growth) and Bioaugmentation (meaning the addition of living cells capable of degradation) studies have enjoyed a heavy presence in literature and reviews of these technologies focusing on the technical aspects are very few if at all available. At times, nutrient application alone or augmenting with microbes is not sufficient enough for remediation leading to a simultaneous approach. Recent studies show that a combination of both approaches is equally feasible but not explicitly more beneficial. Evidently, selection of a technology hinges on site specific requirements such as availability of microorganisms capable of degradation in sufficient quantities, nutrient availability to support microbial growth and proliferation as well as environmental parameters such as temperature in combination with duration of exposure.
    [Show full text]
  • Bioaugmentation for the Remediation of Pesticide- Contaminatted Soil with Microorganisms Directly Enriched in Soil Or Compost
    BIOAUGMENTATION FOR THE REMEDIATION OF PESTICIDE- CONTAMINATTED SOIL WITH MICROORGANISMS DIRECTLY ENRICHED IN SOIL OR COMPOST DISSERTATION Presented in Partial Fulfillment of the Requirements for the Degree Doctor of Philosophy in the Graduate School of The Ohio State University By Sang-Jun Kim, B.S., M.S. ***** The Ohio State University 2003 Dissertation Committee Approved by Dr. Warren A. Dick, Advisor Dr. Edward McCoy Dr. Fredrick C. Michel, Jr. Advisor Dr. Lynn B. Willett Environmental Science Graduate Program ABSTRACT EPTC (s-ethyl-N,N’-dipropylthiocarbamate) and atrazine (2-chloro-4-ethylamino- 6-isopropylamino-1,3,5-triazine) are commonly used agricultural herbicides. Atrazine, especially, can be found in soils and waters at concentrations that exceed the 3 µg/L health advisory level set by U.S. EPA. Developing an effective inoculum with high activity to bioaugment degradation of EPTC or atrazine in contaminated environments is a goal related to bioremediation of such sites. Direct enrichment of microorganisms in soil capable of EPTC or atrazine degradation was accomplished. The effectiveness of adding these soils (hereafter called ACTIVATED soils) for enhancing the biodegradation of EPTC or atrazine in contaminated soil was evaluated. Effectiveness of compost as an inoculum carrier and stability of ACTIVATED soils and compost under different storage conditions were also tested. EPTC-degrading microorganisms were readily enriched in a Brookston clay loam soil that was sampled from a field previously treated with EPTC, and then air-dried and stored at room temperature for 14 years. The most probable number (MPN) method revealed that the number of EPTC-degraders increased by about 3 logs of magnitude after a 7 day water pretreatment followed by a single treatment with EPTC at a rate of 20 mg/kg ii soil.
    [Show full text]