PHYTOREMEDIATION FIELD STUDIES DATABASE for
	CHLORINATED SOLVENTS, PESTICIDES. EXPLOSIVES, and METALS	

                             TABLE OP CONTENTS

 1.  Objectives	1
    1.1. Scope of Project	„	1
    1.2. Requirements	1
    1.3. Concept of Operation	 1
 2.  Introduction	2
    2.1. Phytoremediation	2
       2.1.1. What is Phytoremediation?	2
       2.1.2. History	2
       2.1.3. Advantages and  Disadvantages	..2
       2,1.4. Use in a Treatment Train	3
       2.1.5. Cost	4
    2.2. Contaminant Information	5
       2.2.1. Chlorinated Solvents	5
       2.2.2. Pesticides	7
       2.2.3. Explosives	11
       2.2.4. Metals	12
 3.  Is Phytoremediation Right for Your Project?	14
    3.1. Site Characteristics	14
       3,1.1. Site Characterization	14
          3,1.1.1.Contaminant	14
          3.1.1.2.Site Area and Activities	15
          3.1.1.3.Geological and Hydrological Conditions	15
          3.1.1.4.SoilType	15
       3.1.2. Climate	16
       3.1.3. Time Constraints	16
    3.2. Plant Considerations 	16
       3.2.1. Plant Selection	16
       3.2.2. Types	16
       3.2.3. Phytotoxicity and Treatability Studies	17
       3.2.4. Root and Rhizosphere	17
       3.2.5. Planting Methods	18
       3.2.6. Native vs. Non-Native Species	18
       3.2.7. Plant Specificity	19
       3.2.8. Transgenics	19
    3.3. Agronomic Considerations	20
       3.3.1. Plant Age and Metabolic Status	20
       3.3.2. Amendments	20
       3.3.3. Other Agronomic Issues	20
    3.4. Regulatory Considerations	21
    3.5. Ecological and Social Considerations	21
    3.6. Operation and Maintenance	22
    3.7. Performance Monitoring	23
 4.  Database	24
    4.1. General Layout	24
                                         in

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                 PHYTOREMEDIATION FIELD STUDIES DATABASE for
	CHLORINATED SOLVENTS, PESTICIDES. EXPLOSIVES, and METALS	

   4.2. Soil and Climate Characterizations	24
5. Conclusion	25
   5.1. Summary	25
       5.1.1.  Chlorinated Solvents	25
       5.1.2.  Pesticides	25
       5.1.3.  Explosives	25
       5.1.4.  Metals	25
   5.2. Outlook	26

Appendices	27
A. .Chlorinated Solvent Database	28
B. Pesticides Database	83
C. Explosives Database	103
D. Metals Database	120
E. USDA Soil Classification System	162
F. Climate Table	164
G. Resources	169
H. References	170
                                       IV

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
 	CHLORINATED SOLVENTS, PESTICIDES, EXPLOSIVES, and METALS


                                 List of Tables


Table 1. Phytoremediation Advantages and Disadvantages	3

Table 2. Cost Comparisons: Phytoremediation vs. Traditional Technologies	5

Table 3. Common Chlorinated Solvents	6


Table 4. Common Pesticides	9

Table5. Common Explosives	11

Table 6. Potential Human Health Effects of Metals	13

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
  	CHLORINATED SOLVENTS, PESTICIDES, EXPLOSIVES, and METALS	

                                  1. OBJECTIVES

1.1 Scope of Project
The scope of this project is to compile a listing of sites where field-scale phytotechnologies have
been applied to contain and remediate chlorinated solvents, pesticides, explosives and heavy metals
in contaminated soil and groundwater. Phytomechanisms included in this project shall include
phytoaccumulation, phytoextraction, rhizofiltration, phytostabilization, rhizodegradation,
phytodegradation, phytovolatilization and hydraulic control. Older phytoremediation databases will
be updated and appended by information extracted from government internet sources, literature
searches and personal communication with site contacts.

1.2 Requirements
The following criteria have been set for the database:
1. Project scale shall be demonstration, pilot or full-scale. Laboratory, bench or greenhouse
   scale phytoremediation research shall not be included.
2. Phytoremediation installations of constructed wetlands sites, landfill vegetative cover sites,
   and riparian buffers shall be excluded from the database.
3. Media type shall be limited to soil and groundwater. Wastewater, surface water, sediment,
   and sludge applications shall not be included.
4. Vegetative types include all members of the plant kingdom and fungi.

1.3 Concept of Operation
The purpose of this compilation is to provide an understanding of the successes and failures of
phytoremediation installations to-date. This paper will serve as a reference for federal, state, and site
managers and others to compare their site with others having similar conditions in order to support
the decision of whether or not to use phytoremediation as a treatment technology. A spreadsheet has
been selected as the layout for the database in order to accommodate public navigation. Entries in
the database shall attempt to summarize the relevant logistics, successes and failures of each site by
defining twenty-one fields for each. These elements include:

1.       Site Name                          12.      Project Scale
2.       Site Location                       13.      Project Status
3.       Contaminant                        14.      Cost
4.       Vegetation Type                    15.      Funding Provider
5.       Planting Descriptions                16.      Initial Concentrations
6.       Media Type                         17.      Final Concentrations
7.       Site Characterizations               18.      Lessons Learned
8.       Evapotranspiration Rates             19.      Comments
9.       Climate                             20.      Primary Contacts
10.       Phytomechanisms                   21.      Citation
11.       Operation & Maintenance

Each site profile will allow users to quickly determine the nature of the site and the success of
the technology while also providing avenues to pursue should they want further site
information.

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
           CHLORINATED SOLVENTS. PESTICIDES, EXPLOSIVES, and METALS
                                  2. OVERVIEW
2.1 Phytoremediation
2,1.1 What Is Phytoremediation?
Phytoremediation is the use of vegetation and its associated microorganisms, enzymes and
water consumption to contain, extract or degrade contaminants from soil and groundwater.
Both organic and inorganic contaminants can be successfully contained or degraded using
Phytoremediation in a variety of media (i.e. soil, sediment, sludge, wastewater, groundwater,
leachate and air) (Susarla, 2002). The mechanisms of phytoremediation include:
  •  Phytoextraction - removal and storage of contaminants from the media into the plant
     tissue;
  •  Rhizodegradation - degradation of contaminants by microorganisms in the soil zone that
     surrounds and is influenced by the roots of plants, also known as the rhizosphere;
  •  Phytodegradation - degradation of contaminants within the plant tissue;
  •  Phytostabilization - isolation and containment of contaminants within soil through the
     prevention of erosion and  leaching;
  •  Phytovolatilization - uptake and transpiration of contaminants from the media through
     the plant tissue into the atmosphere; and
  •  Hydraulic Control - containment of contaminants within a site by limiting the spread of a
     contaminant plume through plant evapotranspiration.

In depth details on phytoremediation mechanisms have been thoroughly documented in past
literature and are not the focus of this document (McCutcheon, 2003).

2.1.2 History
The concept of using plants to clean and restore soil and wastewater has been employed for
over 300 years. Numerous bench-scale studies have been performed to determine plant
toxicities and contaminant uptake abilities. In order for phytoremediation to achieve
acceptance as a remedial method,  field-scale applications need to be performed and
documented. Constructed wetlands and vegetative covers have been extensively applied in the
field to demonstrate their ability to remediate contamination and their data has been well
documented (McCutcheon, 2003). More recently, field-scale  studies of groundwater and soil
plantations have been performed to determine their effectiveness in remediating contamination.
The purpose of this paper is to document groundwater and soil plantation applications and their
results, so that the information will be useful in assessing the feasibility of phytoremediation as
a remedial technology for a site.

2.1.3 Advantages and Disadvantages
Phytoremediation, like other technologies, has both advantages and disadvantages associated
with it as shown in Table  1. Advantages and disadvantages are not ranked in any order. The
weight each  element carries will vary with each site.

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
           CHLORINATED SOLVENTS, PESTICIDES, EXPLOSIVES, and METALS
Table 1. Phytoremediation Advantages and
Disadvantages (ITRC, 2004; EPA, 2001)
                Advantages
               Disadvantages
     Cost reduced over traditional methods
     Low secondary waste volume
     Improved aesthetics
     Habitat creation - biodiversity
     Green technology
     More publicly accepted
     Provide erosion control
     Prevent runoff
     Reduce dust emission
     Reduce risk of exposure to soil
     Less destructive impact (applied in-situ)
 •  Long remediation time requirement
 •  Effective depth limited by plant roots
 •  Phytotoxicity limitations
 •  Fate of contaminants often unclear
 •  Climate dependent/variable
 1  Seasonal effectiveness
 •  Potential transfer of contaminants (i.e. to
    animals or air)
 •  Harvesting and disposal of metals in
    biomass as hazardous waste may be
    required, although generally not
 •  Larger treatment footprint	_^
Not all listed advantages and disadvantages are specific to phytoremediation. Footprint size
limitations may affect all remediation technologies. Advances in technology have been able to
alleviate some of the disadvantages. Deeper root depths are achievable today than in the past
due to engineered planting methods (see section 2.2.5). Phytotoxicity has become less of an
issue as genetically modified plants (see section 2.2.7) have been developed to withstand
higher concentrations of contaminants. More disadvantages may be overcome as the
technology progresses.

2.1.4 Use in a Treatment Train
Though not always used as a stand alone technology, phytoremediation can still be a benefit to
many hazardous waste sites. Few hazardous waste sites apply phytoremediation as the sole
treatment method. The technology is often applied in conjunction with other traditional
methods or as the final phase of a treatment train after contaminant concentrations have been
reduced.

Phytoremediation can be used  as part of a treatment train when time constraints require other
methods to be employed to achieve a remediation goal in a short period of time. This usually
occurs when high contaminant concentrations in sensitive areas (i.e. near drinking water
sources) require quick reduction. A series of remediation efforts may be undertaken to reduce
the concentrations to an acceptable level before applying phytoremediation as the last
"polishing step" to remediate and contain low level concentrations.

Phytoremediation can also be applied in conjunction with other technologies to achieve a
treatment goal. The natural solar-powered pumping of deep rooted trees may need to be
coupled with traditional pump-and-treat systems to maintain  treatment rates during the less
effective growing months of the winter season. Vegetation may also be planted around site
perimeters and "hot spots" to maintain hydraulic control and  prevent contamination migration,
while traditional methods are applied to remediate the source. Research on the  addition of

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
 	CHLORINATED SOLVENTS. PESTICIDES, EXPLOSIVES, and METALS	

inorganic, organic and bio-amendments in conjunction with phytoreinediation has also shown
promising results (Kelley, etal, 2000).

2.1.5 Cost
The first costs incurred when approaching any hazardous waste site are those of site
assessment. Regardless of the technology applied, the nature and extent of contamination,
hydrological and geological characteristics and site characteristics must all be assessed. Costs
incurred during this phase are similar for all technologies. Beyond site assessment,
phytoremediation will have unique costs associated with it. These cost considerations can be
divided into four primary categories: (1) Design, (2) Installation (3) Operation and
Maintenance, and (4) Sampling and Analysis.

Design considerations include feasibility studies, plant selection and the associated engineering
costs. Land obstructions at the site may have to be incorporated into the design or removed.
Green house studies or pilot scale testing may be needed to determine which plants to use and
assess the possibility of phytoremediation as a treatment option for the site. Like all designs,
the salaries of engineers performing conceptual work for the site will be the dominant cost in
the design phase.

Installation costs include site preparation, soil preparation, materials and labor. In order to
prepare the site, it may need to be cleared, leveled or fenced in. Soil preparation may involve
pH adjustment, nutrient addition or tilling. Site and soil preparations will require labor and
materials including heavy equipment, organic matter, irrigation systems, plant stock (including
10-20% excess for replanting needs (ITRC, 2004)) and vector protection materials for the
plants.

Operation and Maintenance (O&M) costs will  include monitoring equipment, power sources,
maintenance for the equipment and labor are included. Specific O&M requirements for
phytoremediation are detailed in section 2.5 of this document.

Sampling and Analysis costs may dominate the overall cost of the project due to the length of
time monitoring is required and the extent of data necessary. Costs include labor or machinery
to  collect samples and lab work fees associated with analyzing samples. Data collected during
sampling and analysis is crucial for thorough documentation of site progress and the
performance of phytoremediation as a new technology. The EPA is collaborating with state
and federal partners on implementing a streamlined approach to sampling, analysis and data
management methods. This approach, called the Triad Approach, has the potential to reduce
costs associated with sampling and analysis (EPA, 2004).

The costs associated with these four categories are relatively small compared to those of
traditional remediation technologies. This is especially true in the operation and maintenance
phase where the primary factor in cost reduction is the energy source of the operating systems.
Traditional systems utilize electric power, at a substantial cost, to pump water, whereas
phytoremediation systems take advantage of free solar energy. Individual sites will vary in cost
regardless of the technology being applied. In general, phytoremediation is a low cost
alternative to traditional methods as can be seen in the cost estimates of Table 2.

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
           CHLORINATED SOLVENTS, PESTICIDES, EXPLOSIVES, and METALS
Table 2. Cost Comparisons; Phytoremediation vs. Traditional Technologies
Traditional
Method
Pump and Treat
Conventional
Technology
Traditional
Cuib and Gutter
Standard
Landfill Cap
Activated
Carbon System
Pump & Treat/
Iron Barrier
Flushing/
Vitrification
Scenario
1-acre site
with 20-foot-
deep Aquifer
Army
Ammunition
Plant
SEA Streets
Runoff Buffer
Landfill
Vegetative
Cap - College
Park
Army
Ammunition
Plant - Milan
PCEin
Groundwater
Metals in
Soils
Estimated Cost
Traditional
Method
$660,000
$1 trillion
$1 million
$10 million
$4.00/1 000 gal
8.90/5.30
$/ 1000 gal
75-210/300-500
$/Ton
Phytoremediation
$250,000
$1.8 million
$850,000
$3-4 million
$1.80/1000 gal
$2.00/1000 gal
$25-100/Ton
Reference
Gatliff, E.
(1994)
Matso, K.
(1995)
1TRC
(2004)
ITRC
(2004)
ITRC
(2004)
Schnoor
(2002)
Schnoor
(2002)
2.2 Contaminant Information

The database contained in this document focuses on four of the major contaminant groups
found at hazardous waste sites.

2.2.7 Chlorinated Solvents
The term chlorinated solvents refers to a family of colorless, liquid-phase hydrophobic
organics containing one or more chlorine atoms. Most chlorinated solvents are only slightly
soluble in water and, with the exception of vinyl chloride, have densities greater than that of
water as shown in Table 3. This combination leads to their formation of dense non-aqueous
phase liquid (DNAPL). Chlorinated solvent plumes tend to take a long time to remediate when
DNAPL is present, because it acts as a slow releasing, continuous source. Common uses of
chlorinated solvents include drycleaning operations, degreasing operations, polymer
manufacturing and as a chemical intermediate. Because of their wide use, chlorinated solvents
dominate the listings of hazardous waste at sites nation wide, with trichloroethylene (TCE)
present at 40% off all Superfund sites in the United States (McCutcheon, 2003; USGS, 2004a).
Contamination of soil and groundwater with chlorinated solvents is largely due to accidental
spills and poor handling and disposal practices prior to regulation of the chemicals.

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
           CHLORINATED SOLVENTS, PESTICIDES, EXPLOSIVES, and METALS
The primary chlorinated solvents at hazardous waste sites are trichloroethylene (TCE),
perchloroethylene (PCE) and polychlorinated biphenyls (PCBs), with TCE and PCE being the
most dominant (USGS, 2004a). TCE is primarily used as a metal cleaning agent and in
specialty adhesives. It is a probable carcinogen and can affect kidneys, liver, lungs, and heart
rate. PCE is primarily used as a drycleaning and metal cleaning agent. PCE is not classified as
a carcinogen but has been known to  affect the central nervous system and cause irritation of the
skin, eyes, and upper respiratory system (Evans, 2000). PCBs are synthetic oils that do not
readily react at room temperature. They are primarily used as coolants and/or insulators and
were previously used as a spray to control dust on dirt roads (ASTDR, 2004). PCBs are
classified as probable carcinogens by the EPA and the International Agency for Research on
Cancer. PCB contamination is an ecological concern, because by-products  from burning them
at low temperatures are carcinogenic and their presence in the food chain has affected eggshell
formation in birds (ASTDR, 2004).

Traditional methods for remediating chlorinated solvent contamination include natural
attenuation, soil vapor extraction, air sparging and pump and treat. Phytoremediation
mechanisms that have been successful  in containing and/or remediating chlorinated solvents
include rhizodegradation, phytodegradation, phytovolatilization and hydraulic control using
hybrid poplar and  willow trees as can be seen in the Database of Chlorinated Solvent
Phytoremediation  in Appendix A of this document.

Table 3. Common Chlorinated Solvents
Compound Name
Carbon Tetrachloride
Chloroform
3,3-Dichlorobenzidine
1 , 1 -Dichloroethene
cis-l,2-Dichloroethene
trans- 1,2-
Dichloroethene
1,1-Dichloroethane
1 ,2-Dichloroethane
Methylene Chloride
Perchloroethylene
Polychlorinated
Biphenyls
1,1,1 -Trichloroethane
Chemical
Formula
ecu
CHCb
C,2H10C12N2
C2H2C12
C2H2C12
C2H2C12
C2H4C12
C2H<}Cl2
CH2C12
C2CU
*
C2H3C13
MW
(g/mol)
153.823
119.3779
253.1304
96.9438
96.9438
96.9438
98.9596
98.9596
84.9328
165.834
*
133.404
Density
(g/mL-
20°C)
1.594
1.498

1.213
1.284
1.257
1.176
1.253
1.325
1.623
*
1.3376
Solubility
(g/lOOmL-
20°C)
0.08048
0.795
0.00123
0.225
0.08
0.63
0.506
0.8608
1.32
0.015
*
0.1495
Log Kow
2.64
1.97
3.21,3.5
1.32
1.86
2.09"
1.79
1.48
1.3
3.4
*
2.49

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
           CHLORINATED SOLVENTS, PESTICIDES, EXPLOSIVES, and METALS
Compound Name
1,1,2-
Trichloroethane
Trichloroethylene
Vinyl Chloride
Chemical
Formula
C2H3Cl3
C2HC13
C2H3C1
MW
(g/mol)
133.404
131.388
62.4987
Density
(g/mL-
20°C)
0.442
1.462
0.9106
Solubility
(g/lOOmL-
20°C)
1 .441 1
0.11
0.11
LogK«w
2.42
2.42
1.36
Data for this table extracted from the MIST Chemistry Webbook, Cambridge Chemfinder, the Agency for Toxic Substances and Disease
Registry (ATSDR) ToxFaqs™ and Pankow and Cherry ( 1 996)
* 209 possible PCBs. See the ATSDR internet resources at http://www.atsdr.cdc.gov/toxfaq. html for data.
recommended.
Tree core sampling is an emerging technology that shows promising use as a tool to detect the
presence of chlorinated solvents at sites. Researchers have been investigating the concentration
of chemicals in tree trunks since 1990 (Vroblesky, 1990). Recently, the analysis of tree cores
has gained interest in the field of phytoremediation as a low-cost and easily employable
method to assess contamination presence. Core samples are collected from trees using a small
borer and quickly placed in septum-capped vials to minimize loss of contaminant to
volatilization. Vials are stored overnight at room temperature to allow diffusion of the volatile
organic compounds from the core into the vial headspace. Headspace samples are analyzed and
compared to standards using gas chromatography. Concentrations of the contaminants in the
core are determined by assuming partitioning of contaminants from the cores is similar to that
between air and water and taking into account recent findings on partitioning between air/wood
and wood/water. Studies at the Riverfront Superfund Site show a strong relationship between
contaminant concentrations in trees and shallow soils but a weak one between trees and
groundwater (USGS, 2004b).

2.2.2 Pesticides
Pesticides are defined by the EPA as  any substance or mixture of substances  used for
preventing, destroying, repelling, or mitigating any pest. The term is used broadly to include
herbicides, fungicides, and other pest-control substances. In 1998 and 1999, world pesticide
usage exceeded 5.6 billion pounds. US pesticide usage exceeded 1.2 billion pounds (EPA,
2002), and pesticides were applied at over 900,000 farms and 70 million households
(Delaplane, 2000). Heavy usage over the years (mostly via direct land application) of some of
the more persistent pesticides has resulted in their ubiquitous dispersal, most typically in
aquatic environments (Chaudhry, 2002). For example, traces of a number of organochlorine
pesticides have been found in Arctic environments where no previous application has occurred
(Oehme, 1991).

EPA regulates pesticides because of risks that vary considerably depending on the toxicity of
chemical components and dosage. For example, the most widely used class of pesticides,
organophosphates, is implicated in a number of nervous system ailments and is first among
pesticides most often implicated in symptomatic illnesses. Organophosphates, however, are
typically not persistent in the environment (EPA, 1999).  On the other hand, organochloride
insecticides can be extremely recalcitrant. Several have had production curtailed or been

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                  PHYTOREMEDIATION FIELD STUDIES DATABASE for
 	CHLORINATED SOLVENTS, PESTICIDES, EXPLOSIVES, and METALS	

banned due to deleterious environmental and health effects. Some especially recalcitrant
pesticide pollutants, including aldrin, chlordane, DDT, dieldrin, endrin, heptachlor, toxaphene,
mirex, and hexachlorbenzene, were placed on the 2001 Convention on Persistent Organic
Pollutants "dirty dozen" list to immediately address regulatory concerns. Some properties of
more commonly remediated pesticides, including persistence, Kow, and health effects, are
shown in table 4 on the next two pages.

Pesticide persistence in the environment depends on various chemical factors specific to
the contaminant, such as volatility, solubility, chemical reactivity, soil-water (K
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             PHYTOREMEDIATION FIELD STUDIES DATABASE  for
     CHLORINATED SOLVENTS. PESTICIDES. EXPLOSIVES, and METALS
2.2.3 Explosives
The term explosive refers to prepared chemicals subject to a rapid chemical reaction that
produce or cause explosions. The three main classes of explosives are nitroaromatics,
nitramines and nitrate esters. Nitroaromatics are characterized by an aromatic ring and nitro
groups. The electronegativity of the nitro groups prevents explosives from readily falling
under electrophilic attack. For this reason they are generally non-hygroscopic, insoluble in
water and do not readily react with metals. Common uses of explosives include military
weapons and pyrotechnic shows. Table 5 lists common explosives and some of their
properties.

Contamination of soil with explosives is largely due to manufacturing, storage, testing and
inappropriate waste disposal of explosive chemicals. The primary explosives at hazardous
waste sites are 2,4,6-trinitrotoluene (TNT), hexahydro-l,3,5-trinitro-l,3,5-triazine (Royal
Demolition eXplosive-RDX) and octahydro-l,3,5,7-tetranitro-l,3,5,7-tetrazine (High Melting
eXplosive-HMX). TNT is a nitroaromatic constituent of many explosives. In a refined
form, TNT is stable and can be stored over long periods of time.  It is relatively insensitive
to blows or friction. It is readily acted upon by alkalis to form unstable compounds that are
very sensitive to heat and impact. Health effects due to exposure  to TNT include anemia,
abnormal liver function, skin irritation, and cataracts (ASTDR, 2004). RDX is a nitramine
widely used as an explosive and as a constituent in plastic explosives. RDX can cause
seizures when large amounts are inhaled or eaten. Long-term health effects on the nervous
system due to low-level exposure to RDX are not known. HMX is a nitramine that
explodes violently at high temperatures. It is used in nuclear devices, plastic explosives and
rocket fuels. Insufficient studies on the effects of HMX to the health of humans and
animals have been performed.

Incineration, landfilling and pump and treat systems are traditional methods applied to
remove explosives contamination from soil and groundwater. These approaches are
expensive and can cause air pollution with ash generation. Phytoremediation mechanisms
that have been successful in containing and/or remediating explosives contamination
include phytoextraction, phytodegradation and phytostabilization using tobacco,
periwinkle, and parrot feather plants in constructed wetlands (Bhadra, 1999; Wayment,
1999; Hughes, 1997).

  Table 5. Common Explosives
Compound Name
2,4-Dinitrotoluene
(2,4DNT)
2,6-Dinitrotoluene
(2.6DNT)
2-nitrotoluene
4-nitrotoluene
Hexahydro- 1 ,3,5-trinitro-
l)3,5-triazine(RDX)
Chemical
Formula
C7H6N204
C7H6N204
C7H7NO2
C7H7N02
C3H6N606
MW
(g/mol)
182.1354
182.1354
137.1378
137.1378
222.117
Density
(g/mL-208C)
1.521
1.2833
1.163
1.392
1.82
Solubility
(g/100mL-20°C)
0.027
0.0182
0.06
<0.1
Insoluble
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Compound Name
Octahydro-1,3,5,7-
tetranitro-1,3,5,7-
tetrazocine (HMX)
Tetryl
2,4,6-trinitrotoluene
(TNT)
Chemical
Formula
C4H8N808
C7H5N508
C7H5N306
MW
(g/mol)
296,156
287.1452
227.133
Density
(g/mL-20°C)
1.90

1.64
Solubility
(g/100mL-200C)
Insoluble
0.02
0.01
  Data for this table extracted from the NIST Chemistry Webbook, Cambridge Chemfinder and the Agency for Toxic Substances and
  Disease Registry internet resources.
2.2.4 Metals
Metals include any of the class of chemical elements of atomic number 20 and greater with
metallic luster, ductility, and the ability to conduct heat and electricity. Although metals are
naturally present in the Earth's crust, concentrated metal pollutants enter the environment
in several ways, primarily though the burning of fossil fuels, as a result of mining and
smelting activities, from the application of pesticides and fertilizers, and via sewage and
municipal wastes. Metals in soils can exist as free ions, soluble complexes, bound to
organics, precipitated or insoluble compounds (i.e. as oxides, carbonates, and hydroxides),
or in silicate minerals (Salt, 1995).

Although small amounts of various metals are necessary for cell maintenance, metals can
be toxic to both plants and animals in large amounts. Table 6 shows common metal
pollutants and their health effects. Due to their prevalence, toxicity, and exposure potential,
several of these metals are found in the top 20 on the 2003 CERCLA Priority List of
Hazardous Substances, including arsenic (ranked first), lead (ranked second), mercury
(ranked third), cadmium (ranked seventh), and chromium (ranked seventeenth) (CERCLA,
2003).

Traditional methods of mitigating metal contamination in soils include various isolation,
extraction, immobilization, and toxicity reduction methods, including physical barrier (i.e.
concrete, steel) isolation; chemical solidification/ stabilization; hydrocyclone, fluidized
bed, or flotation processes; electrokinetic processes; soil washing; and pump-and-treat
systems (Mulligan, 2001).  Phytoremediation presents itself as a low-cost, solar-powered,
environmentally-friendly alternative to methods such as extraction and pump and treat
systems, which can be prohibitively expensive, and soil washing, which can reduce the
fertility and bioactivity of soils (Datta, 2004). Because metals are generally non-
biodegradable, phytoextraction is the most common mechanism of metals
phytoremediation, although both phytovolatilization (i.e. for Hg, Se, As) and
phytostabilization mechanisms occur. In general, metal uptake and phytoextraction
coefficients decrease in the order Cr6+ > Cd2+- > Ni2+ > Zn2+ > Cu2+ > Pb2+ > Cr 3+
(EPA, 2000).

Although the first metal-hyperaccumulating plants were identified in the mid-1970s, this
information has only recently been explored  for purposes of remediation. A 1989 Baker
review of terrestrial hyperaccumulators and a 2003 Reeves review of over 30 years' work
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on tropical hyperaccumulators by Robert Brooks and his colleague, catalogue many of the
known species able to extract metals (including arsenic, cadmium, chromium, copper,
cobalt, iron, manganese, nickel, lead, zinc). Yet despite the breadth of morphological/
geographical information now available for over  400 identified hyperaccumulator species,
most plants are restricted to highly metaliferous,  ultramafic (igneous, iron and magnesium-
rich) soils and tropical environments, of relatively small biomass and slow-growing
(Pulford, 2003). Additionally, not much is known about exploiting these properties for
phytoremediation (Reeves, 2003).

The limits of these hyperaccumulator plants are apparent after a review of the very few
field-scale metal phytoremediation successes, despite several years of intense efforts to find
a magic phyto-bullet. Disappointing performance of lead phytoextraction was illustrated at
the Fort Dix Superfund site, where the amount of lead removed was less than the
uncertainty in the heterogeneous soil profile and  less than the amount of unaccounted
"missing" lead (Rock, 2003). Similarly, ineffectiveness of lead removal was concluded at
the Magic Marker Superfund site, where lead concentrations in phytoextracted tissue did
not account for the reduction in soil lead concentrations (Rock, 2003). These inefficacies
have led to current research interests in identifying those genes responsible for metal
resistance and accumulation and in developing enhanced transgenic plants for application
in the field. Recently, Song (2003) explored the effect of inserting yeast proteins into
mouse ear cress (Arabidopsis thaliana) and Gisbert (2003) investigated genetically-
modified shrub tobacco  (Nicotiana glauca), in two independent efforts to develop a lead
and cadmium tolerant plant that may lead to better field success in the future.

One of the most important factors determining metal phytoremediation  success is
contaminant bioavailability. Metal bioavailability is  determined by physical factors
(contaminant coarseness, soil texture, etc.), chemical factors (concentration, speciation, pH,
Eh, cation exchange capacity, acidity, redox potential), and biological factors (plant,
mychorrizal, and microogranism activity) (Ernst, 1996).  Some of these factors can be
altered in the development of a phytoremediation site, such as importing more amenable
soils,  adjusting pH and/or alkalinity, etc. For example, decreasing soil pH generally
increases metal availability, but it is important to make sure plants are able to survive under
the same pH conditions. Competition between metals can also have a profound effect: in
general, increasing the metal loading rate in a soil (i.e. containing cadmium, chromium,
copper, manganese, lead, and zinc) decreases the bioconcentration factor of metals in
plants. (Wang, et al 2002).

  Table 6. Potential Human Health Effects of Metals
Metal
Arsenic
Lead
Mercury
MW
74.92
207.20
200.59
Health Effect
Acute: Lung irritation, nausea, vomiting, blood vessel damage, abnormal hearth rhythm, death.
Chronic: keratoses and skin effects; peripheral vascular disease; hypertension and cardiovascular
disease; cancers of the bladder, kidney, liver, and lung; diabetes mellitus; possible neurological
effects
Affects central nervous and reproductive system, damages kidneys, may cause anemia, decrease
reaction time, cause weakness in fingers, wrists, ankles, and affect memory.
Bronchitis, gingivitis, pulmonary edema, nervous system disorders, and permanent damage to brain,
kidneys, and developing fetus.
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Metal
Cadmium
Chromium
Zinc
Nickel
Silver
Copper
Manganese
MW
112.41
52.00
65.39
58.69
107.87
63.55
54.94
Health Effect
Pulmonary edema, emphysema, anemia, lung cancer, anosmia, kidney disease, fragile bones with
long-term exposure. Acute exposure: lung damage, vomiting, diarrhea, and death
Nosebleed, ulcers, stomach upsets, convulsions, kidney and liver damage, death. Cr (VI) is a
carcinogen.
Comeal ulceration, esophagus damage, pulmonary edema, skin irritation, stomach cramps, nausea,
vomiting.
Dermatitis, pneumonia, lung and nasal cancer, chronic bronchitis, effects on blood and kidneys.
Probable carcinogen.
Blindness, skin lesions, pneumonoconiosis, arygria, lung irritation, stomach pains.
Acute: stomach and intestinal distress, liver and kidney damage, anemia. Chronic: headaches,
dizziness, nausea, diarrhea.
Liver cirrhosis, pneumonia, bronchitis, manganism, respiratory problems, sexual dysfunction
Data for this table extracted from the Cambridge Chemfuider and the Agency for Toxic Substances and Disease Registry internet
Chlorinated solvents, pesticides, explosives and metals are only four of several major
contaminants found at hazardous waste sites and only one of many site characteristics that
define a site. The varying nature of what can be found at a site poses a challenge for
determining whether phytoremediation is a viable remediation technology for any
particular site. The next section of this document details considerations for determining
whether phytoremediation is appropriate for a site.

       3. IS PHYTOREMEDIATION  RIGHT FOR YOUR PROJECT?

3.1 Site Characteristics

3.1.1 Site Characterization
A thorough site analysis that includes contaminant, geological, hydrological, and soil
assessments is essential to determine base line conditions, phytotoxic conditions, the
potential for contaminant removal, and to meet treatment goals (Tsao, 2003). The ITRC has
produced Decision Tree documents (1999,  2001) to aid in the evaluation of a potential
phytoremediation sites, although a brief overview of some important considerations can be
found below.

3.1.1.1. Contaminant
As discussed previously, the nature of the contaminant (recalcitrance, persistence,
bioavailability, etc.) is crucial when developing effective phytoremediation strategies for a
given site. High contaminant concentrations may limit phytoremediation as a treatment
option due to phytotoxicity or the impracticality of using such a slow remediation method.
Additionally, the physical location of the contaminant will determine the efficacy of
treatment. Due to plant root limitations, phytoremediation of soils and sediments is
typically employed for contaminants in the near surface environment within the root zone.
For groundwater treatment, phytoremediation is limited to unconfmed aquifer where the
water table and the contaminant are both within reach of plant roots (either in direct contact
or via transpiration).
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3.1.1.2. Site Area and Activities
Past, current, and future site activities will affect phytoremediation system design. Past site
activities will determine contaminant and soil properties (i.e. quantity, age, and quality) at
the site and existing vegetation may influence the growth and stability of any introduced
phytoremediating plant species. An area assessment will be required to consider the amount
of space available for phytoremediation, to identify any physical obstacles, and to
accommodate any concurrent activities. Chemical, physical, and biological impacts of
vegetation on the site should also be determined. Because phytoremediation is a long-term
remediation process, often on the order of several years, any proposed future site activities
will also need to be considered and integrated into the final system design.

3.1.1.3. Geological and Hydrological Conditions:
Topography of the site will affect surface and subsurface flow patterns and drainage. A
proper evaluation of the hydrologic regime includes measuring recharge, potentiometric
levels, and discharge, and includes a determination of surface and subsurface runoff,
infiltration, and water storage. The remediation of groundwater requires creating a cone of
depression so contaminants can be transported to the plant root zone for treatment. The
goal of hydraulic control is to have plume movement minimized as much as possible,
where infiltration is roughly equal to the amount of evapotranspiration. Runoff and
infiltration controls are necessary to prevent contaminant mobilization. At sites with very
porous soils, lining may be required to control the amount of infiltration. Calculating the
overall water balance of the system may be required to estimate whether phytoremediation
will be effective at controlling contaminant plumes. The use of hydrological models, such
as the USGS groundwater model MODFLOW, can aid in the assessment and
characterization of aquifer and contaminant movement For example, site characterization
and groundwater flow modeling using MODFLOW at the Aberdeen Proving Grounds
found phytoremediation processes  to be more effective than groundwater circulation wells
in the control and removal of dissolved-phase volatile organic compound (VOC) plumes
contaminating the site (Hirsh, 2003).

3.1.1.4. Soil Type
Soil characteristics, such as moisture content, available oxygen, organic matter content,
cation exchange capacity, pH, alkalinity, content, texture (particle size), and temperature
will have significant effects on contaminant mobility and fate. For example, metal
bioavailability in high clay and low organic content soils is decreased. Higher soil cation
exchange capacity indicates greater sorption of metal contaminants. Soil fertility will
determine whether additional fertilizers will be necessary. Soil pH affects metal
contaminant solubility as well as plant growth, and a balance should be met to maximize
both. The importance of soil conditions was made apparent in a recent study by Boyle and
Shann (1998), who compared the growth response of three different plant species
(sunflower, Timothy grass, and red clover) under varying soil conditions (coarse silty loam,
fine clay loam, and fine-silty loam) and found soil type to be one of the most significant
factor in rhizosphere degradation of a pesticide (2,4,5-trichlorophenoxyacetic acid).
Characterization studies to assess horizontal and vertical distributions of soil properties
should be undertaken prior to full-scale implementation.
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3.1.2 Climate
At the macro scale, climate is one of the major factors affecting evapotranspiration rates
and, subsequently, the amount of contaminant that can be contained. Optimal conditions for
maximum evapotranspiration are high water, high solar radiation, high wind speed, warm
temperature, low relative humidity (high vapor pressure gradient), and long growing-
season environments (Vose, 2003). Evapotranspiration is linearly related to precipitation
and the amount of water available in the soil. Solar radiation regulates the opening and
closing of the stomata and wind speed affects convective flow across leaf surface area.
Relative humidity and vapor pressure gradients on the leaf surface will limit the amount of
transpiration. Frost dates serve as limits to effective duration of a phytoremediation season
for most plant species.

3.1.3 Time Constraints
Phytoremediation is a long-term remediation strategy, but the time required varies and is
hard to predict. It requires sufficient time for vegetation to become established and grow to
levels associated with higher transpiration rates. Phytoremediation is also limited by
climate variation and seasonal effects particular to a site, which lengthen the overall time
required. For example, perennial plants require at least a year to establish, and for organic
compounds, at least three or more years are needed to allow for plant stabilization (Davis,
2003). A rough estimate of the clean-up time required can be  extrapolated from calculating
the rate of contaminant uptake by a plant. The uptake rate requires knowing the efficiency
of uptake (i.e. transpiration stream  concentration factor, TSCF), the transpiration rate,  and
the concentration of contaminant in soil solutions (Schnoor, 2003).

3.2 Plant Considerations

3.2. J Plant Selection
Selection of appropriate plants should take into consideration issues of contaminant
tolerances, evapotranspiration rates, climate and weather (e.g. flood, drought) tolerances,
growing season, root depth, and disease and pest resistance. Although no plant protocols
have been established, an integration of this database with others (such as the U.S.
Department of Agriculture [USDA] plants database) can be used to narrow down the
possibilities.

3.2.2 Types
Plants used in phytoremediation include trees, grasses, flowers, and shrubs, and various
aquatic plants. Although nearly all  the phytoremediation sites to date have used terrestrial
plants, several hydroponic and aquatic plant studies have been employed for use in
constructed wetlands and in plant/ phytotoxicity screening to  determine the efficacy of
contaminant uptake from groundwater under idealized conditions. Aquatic plants have
great potential for in situ remediation, such as with the use of constructed wetland
biofilters, however they are not considered any further here. Plant selection requires
demonstrated effectiveness at mitigating the pollutant of concern and a phytotoxicity
evaluation. A perusal of the phytoremediation database shows that the species most
commonly used in field-scale phytoremediation applications are (hybrid) poplar, (hybrid)
willow, cottonwoods, ryegrass, fescue, alfalfa, Indian mustard, and parrot feather. The
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popularity of hybrid poplars is due to their quick growth, deep roots, and extremely high
rates of evapotranspiration. Poplars and other plants, however, vary considerably across
their genus in their phytoremediating abilities (i.e. growth rate, metabolic activity, rooting
characteristics, disease and drought resistance, etc.), so care should be taken when selecting
cultivars that have worked at a site with differing characteristics (Compton, 2003; White,
2003). For heavy metals, accumulator plants typically selected are not only able to tolerate
and accumulate pollutants, but also have high above-and-below-ground biomass and are
fast growing; however, Pulford (2003) proposes using non-accumulator plant species for
heavy metal uptake in arrangement with optimized soil conditions (i.e. chelation) or via
genetically-modified strains.  For organics, vegetation should generally be fast growing,
have high evapotranspiration rates, and transform contaminants to less toxic or nontoxic
forms (ITRC, 1999). For remediation of chlorinated solvents, typically used species include
hybrid poplar and hybrid willow (see database). For munitions, periwinkle (Catharanlhus
roseus) has been successful for munitions, in addition to the parrot feather (Myriophyllum
aquaticum), although hybrid poplar is beginning to emerge as an alternative (Hughes,
1997; Bhadra, 1999; Wayment, 1999). Pesticides are most commonly treated using hybrid
poplars, although various other crop, grass, and colonizing plant species have shown
tolerance and phytoremediating potential in the laboratory,  as summarized by Karthukeyan
et. al (2004).

3.2,3. Phytotoxicity and Treatability Evaluation
Toxicity screening tests are use to determine possible plants for a set of contaminant,
nutrient levels, pH, and salinity conditions. Using these bench-scale pot, hydroponic, or
greenhouse studies is a prerequisite to actual implementation at a contaminated site. When
evaluating plants in phytotoxicity studies, a general rule to follow for organic contaminants
is that plants able to survive 10+ mg/L of organic contaminant are recommended, with
plants surviving 1-10 mg/L conditions as additional possibilities; for inorganic
contaminants, species able to tolerate  100+ mg/L are recommended, with plants surviving
at  10-100 mg/L as additional possibilities (Gatliff, 2004). Treatability studies are used to
estimate the rate of contaminant treatment, to determine fate and transport in the system,
and to develop models and mass balances. In treatability studies under controlled
conditions, it is imperative to replicate site conditions (site soils,  humidity/ water
availability, pH, etc.) as closely as possible. A review of the genetic and molecular basis of
plant tolerance and phytotoxicity was recently undertaken, with special attention to
chlorinated aliphatic compounds and explosives (Medina, 2003). Karthikeyan et al (2004)
recently reviewed the laboratory-scale tolerances of various tree, grass, and crop species to
various pesticide compounds.

3.2.4. Root andRhizosphere
Roots have a variety of functions that include structural support for plants, the uptake of
nutrients and water, and the release of exudates. For phytoremediation, treatment is limited
to the roots' zone of influence and therefore the contaminant depth should not exceed root
depth. For non-woody plants, the effective root depth usually does not extend more than a
couple feet; however, for phreatophytes (i.e. poplar trees) this depth can be extended
significantly by methods of deep rooting. Root exudates also play a crucial role in
rhizosphere phytoremediation processes for both inorganic and organic contaminants.
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Exudates are compounds released from plant roots that stimulate microbial growth and
activity in the rhizosphere. Exudates can also alter soil pH, act as chelating agents, aid in
nutrient recomplex with metals, and degrade organic compounds (Tsao, 2003). Root
turnover is yet another mechanism of adding organic substrate to soils for the stimulation
of microorganisms. Although rhizosphere processes are generally poorly understood,
several plant species (e.g. legumes) are capable of sustaining active microbial populations,
and may be selective in their capacity to degrade certain compounds, such as pesticides
(Karthikeyan, 2004).

Root growth in the contaminant zone is a function of contaminant and water depths,
climate, nutrient availability, water distribution, soil strength, and available oxygen (Negri,
2004). A  few recent studies illustrate the importance of these factors. For example,
Nzengung (2004) observed that available oxygen, nutrients (nitrate), root mortality, and
redox conditions determined whether rhizodegradation of perchlorate in the root-zone was
the favored phytoremediation mechanism. A 2003 study by Keller that compared the ability
of various plant species to extract copper, zinc, and cadmium from soils found that a larger
ratio of root density to above-ground biomass and generally large overall root area were
positive factors. Modulating root temperature by the use of polyethylene mulches for
enhancing cadmium and zinc extraction in potato plants was proposed by Baghour (2002).

3.2.5 Planting Methods
The method of planting will depend on the type of vegetation used in treatment.  For
example, grasses are usually dispersed as seeds, and trees such as poplar are transplanted
from pots as whips or from cuttings. Planting dates are dependent on the climate at a given
site. Seeding methods including depth of sowing, then "pelletizing" of smaller seeds, hand
vs. machine sowing, density and distance between rows have been discussed in the
literature (Angle, 2001). Typically, vegetation is planted at the leading edge of the
contaminant plume, perpendicular to groundwater flow (Ferro, et. al 2003).

If deep rooting is required, poplars and willows are popular phreatophyte choices due to
their natural predisposition to develop roots at greater  depths, especially in porous soils and
arid environments. Rooting below 1 meter usually involves installation in boreholes or
trenches, along with engineered media to direct the root growth. Deep rooting can be
feasibly engineered to depths of up to 40 feet. Engineered media includes backfill material
to maintain favorable root growth conditions, and casings to direct root growth and reduce
the amount of surface water available, as well as short-circuiting, in the system (Negri,
2003). Deep rooting may not always have desired effects. For example, Sung (2003) found
that rooting at depth made no difference in TNT or PBB disappearance rates for
Johnsongrass (Sorghum halapense) and Canadian wild rye (Elymus canadensis).
Additionally, care should be taken to ensure there is a  sufficient lateral root system to
maintain  structural support.

3.2.6 Native versus Non-native Species
Recent legislation, such as two recent Executive Orders (1994, 1999) and the 1996 Invasive
Species Act and the 2000  Plant Protection Act, limit the introduction of invasive or non-
native plant species to areas where they are not indigenous. In addition to regulatory
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reasons, indigenous species are recommended over non-native species for use in
phytoremediation projects as they involve the least amount of human and ecological risk.
Native species are often better adapted to the conditions of the environment (i.e. adapted to
soil conditions and are tolerant to the hydraulic regime), require less maintenance,
monitoring, and control, have lower energy requirements, and involve less residual disposal
(Marmiroli, 2003; Compton, 2003). The hierarchy for selecting plants is native species >
hybrid species > non-native/ introduced species > engineered species (ITRC, 2004).

3.2.7 Plant Specificity
Although most phytoremediation sites are developed assuming a rigid plant-contaminant
specificity, there have been some interesting developments in studies on plants that are able
to remediate more than one class of pollutant. For example, a field plot study by Martina et
al (2003), determined concurrent uptake  of chlordane and heavy metals (As, Cd, Pb, Zn) by
Zucchini (Cucurbita pepo) and spinach (Spinachia oleracea). The possibility of one plant
remediating multiple categories of contaminant should be accounted for in project design to
ensure that remediation objectives are met.

3.2.8 Transgenics
Genetic modification  of a plant involves  insertion of a piece of foreign DNA (e.g. for
enhanced tolerance or accumulation) into the genome of the species of interest. Wolfe and
Bjornstad (2002) hypothesize that phytoremediation using genetically-engineered plants
would create more opposition and controversy than non-genetically engineered plants
based on past public responses to the biotechnology applications.
The negative perceptions and widespread resistance  to the use of genetically-engineered
plants can be attributed to "the failure of the biotechnology industry to educate the
community about the  risks and benefits of transgenic technology," which Linacre (2003)
suggests can be  overcome by adopting a combined risk assessment (i.e. defining risks,
associated probabilities, and dose/consequences), risk management, and risk
communication  strategy.

Despite the aforementioned social obstacles, research into transgenic plants has accelerated
and modified, phytoremediating plants have been introduced at field-scale. While most past
transgenic research has focused on developing hyperaccumulators or plants with enhanced
biodegradation,  some recent research has been undertaken to develop genes for "anti-
contaminant/antibody fragments" capable of improved pollutant-accumulation (Chaudhry,
2002).

Genetically-modified lead accumulators were previously discussed, but a sampling of some
recent GMO (genetically-modified organism) research follows: Transgenic mouse ear cress
(Arabidopsis thaliana) has recently shown to hyperaccumulate arsenic in laboratory studies
(Dhankher et. al, 2002). And in October 2003, the first commercial application of
genetically modified species for phytoremediation was planted at a Danbury, CT
brownfields site. In this particular case, bacterial genes that encode enzymes for conversion
of toxic methyl mercury to volatile elemental mercury were inserted into cottonwood trees
(APGEN, 2003).
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3.3 Agronomic Considerations

3.3.1. Plant Age and Metabolic Status
While water content, diurnal cycles, temperature, and periods of dormancy are also
important to determine metabolic status, frost dates for a given site is one of the largest
determining factors (see database). Plant age determines plant size and overall leaf surface
area, which in turn is responsible for evapotranspiration rates. For example, poplar
transpiration rates are around 1.6-10 gallons per day (gpd) during the first two years, but
transpiration rates increases to between 13-200 gpd after 10 years (ITRC, 2004). Plant age
also determines contaminant tolerance; for example, in a study by Peralta-Videa (2003), the
phytotoxicity of metals (i.e. Cd, Cu, Zn) to alfalfa plants decreased with plant age.
Deciduous trees are dormant for a large part of year, while conifers continue to transpire at
a reduced rate throughout the winter season and have higher overall rates of
evapotranspiration due to higher total leaf surface area (Vose, 2003).

3,3.2. Amendments
The addition of inorganic, organic, and bio-amendments are often used to  enhance
phytoremediation, and there are a few recent applications of these to pesticides. Microbe-
mediated rhizosphere degradation is a principal phytoremediation mechanism, and often
the major limiting factor of pesticide biodegradation is a deficient population of
microorganisms (Olson, 2003). One recent study showed that bacterial (Actinomycete)
inoculants in soils increased the amount of 1,4-dioxane in soil that was mineralized,
although their addition had little effect on the total amount of dioxane removed by hybrid
poplars (Kelley et ai, 2000). Laboratory studies have also shown that strains of
Agrobacterium tumefaciens were capable of increasing root mass and stimulating PCB
uptake by plants, an amendment method which may be applicable to pesticide remediation
in the future (Chaudhry, 2002; Gleba, 1999).

Similarly, metal phytoextraction can be used as part of a treatment train or in combination
with other remediation technologies. Popular alternatives include the addition of chelating
agents such as EDTA, or organic acids such as citric acid that mimic natural plant excretion
of organic ligands (Romkens, 2002). However, care must be taken when adding chelates
and other amendments, because they may lead to uncontrolled releases and/or require
costly engineered barriers to be put in place (Rock, 2003). Amendments should be
evaluated in bench-scale studies prior to field application to ascertain optimum conditions.
For example, citric acid may be degraded by microorganisms too quickly to be used in
long-term remediation (Romkens, 2002), or the increased metal bioavailability with
addition of EDTA and citric acid amendments may correspond to high levels of plant
phytotoxicity (Chen, 2001; Turget, 2004). Adding biological amendments such as fungi
and microorganisms, or integrating phytoremediation with another technology (e.g.
electrokinetic remediation) is another possibility.

3.3.3. Other Agronomic Issues
Although monoculture plantations have often  been used in phytoremediation in the past,
there is increasing trend towards incorporating mixed cultures. Monoculture plantations
have the advantage of reduced competition for nutrients and space, and it may be easier to
                                        20

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             PHYTOREMEDIATION FIELD STUDIES DATABASE  for
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control undesirable organisms that do emerge. However, the use of a single plant species
introduces several potential problems. Intensive monoculture cultivation requires high
levels of irrigation, fertilizer, and amendments to sustain plant productivity. Monocultures
are far less resistant to disease and invasive species than mixed cultures. Additionally,
optimization of some phytomechanisras, such as rhizodegradation, requires a diverse and
complex range of species interactions, which cannot occur under a single plant
environment (Olson, 2003). If a mixed culture is used, the potential for alleopathy or
interspecies competition between plants, which may lead to the subsequent inhibition of
one plant, should be evaluated.

Plant rotation is commonly used in agronomic practices to recycle important nutrients in
the soils, reduce the need for fertilizer and other amendments, and to alleviate stresses.
Natural succession often results as an ecological community response to environmental
stresses. Site operators may consider mimicking succession by first introducing a "pioneer"
species to stabilize conditions, then adding a more and more diverse mix of plant species
with time, improving disease and stress resistance (Olson, 2003). Additional agronomic
recommendations include avoiding a grid pattern when planting, allowing for sufficient
space between trees (for maintenance and monitoring activities), and installing monitoring
equipment, drainage systems, etc. prior to planting (Compton, 2003).

3.4 Regulatory Considerations
Phytoremediation as a technology has experienced increased regulatory approval and
standardization, although there are no federal regulations specific to phytoremediation to
date. Regulations posed by the Resource Conservation and Recovery Act (RCRA),
Comprehensive Environmental Response Compensation and Liability Act (CERCLA),
Clean Air Act (CAA), Toxic Substances Control Act (TSCA), Federal Insecticide
Fungicide and Rodenticide Act (FIFRA), Federal Food Drug and Cosmetic Act (FFDCA),
Invasive Species Act, Plant Protection Act, statutes enforced by the USDA and state
statutes must all be upheld when installing a phytoremediation system. USDA and state
statues may govern the plant species used and the extent of vegetation allowed and/or
required. Common issues faced under these regulations include:
•        Transport of contaminants from the subsurface to the surface.
•        Transport of contaminated media off-site
•        Permits to dig on-site
•        Permits to plant
•        Handling of secondary waste/degradation products
Site managers must ensure all actions abide by the stipulated regulations and that proper
permits  are obtained.

3.5 Ecological  and Social Considerations
It is obvious that success of a phytoremediation project is dependent on various technical
aspects such as site, contaminant, and plant characterizations; equally imperative, yet less
often considered, are numerous social considerations. Some issues that may affect
community acceptability of phytoremediation include site aesthetics, odor production (i.e.
with volatile contaminants), dust from tilling and maintenance, pest attraction, and
production of pollen (i.e. aggravation of allergies). Additional issues may include the
                                        21

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             PHYTOREMEDIATION FIELD STUDIES DATABASE for
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degree of perceived risk (i.e. contaminant concentrations and required length of treatment);
unpredictability (i.e. the dearth of available data and research on this "emerging"
technology); issues of genetic engineering; ecological impacts; the appropriateness of
extrapolating demonstration to full-scale; and linking, or including as a part of a treatment
train, phytoremediation to other, less acceptable technologies or practices. (Wolfe and
Bjornstad, 2002).

There are several ecological concerns to be cognizant of when developing a
phytoremediation site. As discussed previously, introduced species can become invasive if
not controlled properly. Introduced and genetically-modified species can have possibly
deleterious effects on nearby crops if interbreeding between species or cross pollination is
allowed to occur. Monoculture plantations maybe more susceptible to disease, increasing
the possibility of airborne plant diseases that may infect other ecological communities.
Additionally, without proper pest and animal controls in place, bioaccumulated
contaminants in vegetation may be enter the food chain.

Despite the aforementioned concerns, phytoremediation is generally regarded in a
favorable manner because it is a solar-driven "green" technology that concurrently treats
contaminants in situ and improves the aesthetics and habitat of the surrounding area.

3.6 Operation and Maintenance
Because phytoremediation uses living organisms, installations of the technology have
unique O&M requirements when compared to other more traditional remediation systems.
Maintaining a healthy system is crucial to the continuation and effectiveness of the
remediation process. Varying plants, climates, and contaminants may cause a site to have
some of, all of, or additional requirements to those listed here. Some unique operation and
maintenance requirements for a phytoremediation site include:

•       Visual inspections
•       Fertilization
•       Irrigation
•       Weed control
•       Mowing
•       Harvesting
•       Pest Control
•       Replanting

Visual inspections, fertilization, irrigation and pest control are steps taken to ensure plant
growth. Weed control aids in both plant growth and prevention of invasive species
infiltration. Mowing is primarily implemented to facilitate easier monitoring and
maintenance of the site. Harvesting plant tissue removes contaminants that have
accumulated within  the plant tissue. This storage of contaminants can be either a liability or
an asset to a phytoremediation site. If the contaminant is a hazardous waste with no further
use, the tissue must be disposed of as hazardous waste at an additional cost. Some
contaminants accumulated in the plant tissue, such as heavy metals, may be reclaimed and
sold in a practice known as phytomining. In such cases, these "cash crops" can be an asset
                                                       22

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             PHYTOREMEDIATION FIELD STUDIES DATABASE for
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to the project by defraying some of the total cost. Pest control is important to protect both
the livelihood of the vegetation and also of the surrounding wildlife. Animals that eat or
damage the vegetation can destroy plantations, thereby hindering remediation, but they can
also harm themselves if they ingest contaminated plant tissue or water. Replanting is a
maintenance issue necessary to ensure continuous contaminant uptake. Vegetation dies for
several reasons (i.e. damage by animals, insects and weather) and needs to be replanted to
maintain the root mass necessary for contaminant uptake and release of exudates. Dead
plant matter, along with other debris, must be removed from the site. Site cleanup is a
maintenance issue that helps facilitate easy monitoring and implementation of other
maintenance needs. Vigilance, frequent site  visitation, and maintenance during first year of
a plantation is crucial and play a large factor in whether phytoremediating plants become
established or not, with moisture availability and weed control being some of the more
critical requirements (Compton, 2003).

3.7 Performance Monitoring
Some monitoring requirements for a phytoremediation system are similar to those of a
traditional remediation system, such as contaminant concentration and groundwater levels.
Phytoremediation installations also have unique characteristics that require monitoring.
They include:

•        Plant health
•        Root depth and density
•        Evapotranspiration
•        Groundwater levels
•        Tissue sampling
•        Precipitation
•        Soil moisture
•        Microbial characterization

Plant health and root depth and density must be monitored to ensure continuous
contaminant uptake and remediation in the target zone. Evapotranspiration and
groundwater level monitoring, along with tissue sampling, can  aid in confirming
contaminant uptake and hydraulic control. Precipitation, soil moisture and microbial
characterizations are monitored to classify the environment the system is operating  in. This
classification is important for two reasons. Firstly, data collected can be consulted when
failures occur to aid in the determination of  the cause. Notable changes in aspects of the
environment can be investigated as possible remedies to the failure. Secondly,
characterization of the climate is important to thoroughly document successful applications
of phytoremediation.  The varying  nature of site characteristics suggests there is not one
installation to be prescribed for all  sites. Therefore, each site will have different monitoring
requirements.

The site-specific nature of a phytoremediation prescription lends itself towards a need for
thorough documentation of site installations. Experts in the field have given opinions about
the kind of data that should be collected from each site in order for a phytoremediation
database to be useful. The resulting compilation of phytoremediation sites has been
                                         23

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             PHYTOREMEDIATION FIELD STUDIES DATABASE for
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organized into a database for easy navigation and implementation into searchable software
programs if needed.

                                 4. DATABASE

4.1 General Layout
The database is divided into four sections, one for each major contaminant class:
chlorinated solvents, pesticides, explosives, and metals. Appendix A contains site
contaminated with chlorinated solvents, Appendix B contains pesticide sites, Appendix C
contains explosives sites, and Appendix D contains metals sites. Each appendix contains, at
the beginning, a table of contents for every listed individual contaminant that details what
sites contain what contaminant. In the pages following the table of contents, the data
collected for each site have been compiled and are presented in a single page layout.

4.2 Soil and Climate Characterizations
In order to maintain uniformity for the entries in the database, a single classification system
was necessary to define soil and climate characteristics. The need for a single system to be
used in this database resulted in an extensive search and the eventual  selection of one
classification system. The USDA 1993 Soil Survey Manual was used for soil texture
classification, because it contained a manageable range of classification terms. Others soil
classification systems had too many or too few categories to sufficiently characterize soil.
In addition, soil texture classes used in the USDA Manual were identical to those found in
a majority of the existing site literature. The soil texture categories, containing a brief
description, are listed in Appendix E.

Following a review of the available site data and consultation with experts, the critical
climate parameters necessary for phytoremediation site determination were defined. These
parameters include site average temperature ranges, elevation, average annual precipitation,
and frost dates (growing season). The National Oceanic and Atmospheric  Association
(NOAA) Cooperative Institute for Research in Environmental Sciences (CIRES) Climate
Diagnostics Center was the resource used to obtain temperature, elevation and precipitation
data. The primary factor in this decision was the availability of multiple criteria from one
source. Frost date data was taken from the Victory Seeds.com website because of its ease
of use and its reliable source of information. Victory Seeds data comes from the
Climatography of the U.S. No. 20, Supplement No. 1 document released in 1988 by
the National Climatic Data Center, NOAA, and the U.S. Department  of Commerce.

When information for a particular site location was not available, data was taken from the
closest city containing all the existing parameters. A representative list of cities across the
United States, including the four critical climate parameters, can  be found in Appendix F.
t
                                                      24

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             PHYTOREMEDIATION FIELD STUDIES DATABASE  for
     CHLORINATED SOLVENTS. PESTICIDES. EXPLOSIVES, and METALS

                                5. CONCLUSION

5.1 Summary
A summary of findings for each of the four contaminant classes, including the number of
field-scale sites, typical contaminants, most commonly planted species, and cost range of
site implementation and operation, is provided below.

5.1.1 Chlorinated Solvents
Appendix A contains 47 sites that have used phytoremediation to treat chlorinated solvents.
The most common contaminants found at these sites are trichloroethene and
perchloroethene. Hybrid poplar and phragmites are the typical plant species used in
treatment. Total costs for installation, operation, and maintenance of these
phytoremediation sites vary widely, from about $51,000 to $2.1 million per site. The higher
costs associated with some of these sites generally reflect pilot or demonstration sites
where extensive research operations and/or monitoring and are included as part of the total
cost.

5.1.2 Pesticides
Appendix B contains 19 sites for the phytoremediation of pesticides and herbicides. The
most commonly remediated contaminants are atrazine and alachlor. Hybrid poplars are the
most popular vegetation used in treatment. Costs for pesticide phytoremediation range
between $6,000 and  $5.4 million/acre, where the higher costs reflect pilot or demonstration
sites.

5.1.3 Explosives
Appendix C contains 12 field-scale sites that were used to remediate explosives. The most
common explosive contaminants found at these sites are  HMX
(octahydrotetranitrotetrazocine), TNT (trinitrotoluene), and RDX
(hexahydrotrinitrotriazine). Tobacco composting and constructed wetlands are most
typically applied in treatment. Total costs for installation, operation, and maintenance of
these sites vary between $60,000 and $1.8 million.

5.1.4 Metals
Appendix D contains 44 sites for the remediation of metals and metalloids. The most
commonly remediated metals are lead (in the past projects), and arsenic and mercury
(currently). Metal-specific hyperaccumulator plants and poplars are most often planted to
remediate metals contaminated sites. The cost of phytoremediation for these sites ranges
between $5000 and $4 million per acre.

Referring to the compiled data, it can be deduced that no single application of
phytoremediation is  appropriate for all sites. Rather, a prescription must be made based on
a thorough site assessment. Phytoremediation may be the sole solution to a remediation
project in instances where time to completion is not a pressing issue. While
phytoremediation may not be a stand alone solution to all hazardous waste sites, it can
certainly be used as part of a treatment train for site remediation either during peak growing
25
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             PHYTOREMEDIATION FIELD STUDIES DATABASE  for
     CHLORINATED SOLVENTS. PESTICIDES. EXPLOSIVES, and METALS

seasons or as a polishing step to clean up the last remaining "hard to get" low
concentrations.

Phytoremediation is still a new technology looking for industry-wide acceptance. The
number of field sites collected in this project indicates it has received greater acceptance
for chlorinated solvents and metals while just starting to gain acceptance within the
explosives and pesticides domains. Continued bench-scale studies are needed to determine
plant toxicities, degradation pathways and contaminant fates and the resulting field scale
applications are necessary to provide proof the technology works in order for
phytoremediation to be fully accepted by the industry.

5.2 Outlook
The data compiled in this project may have a future as part of a larger database. EPA
Region 5 and EnviroCanada are currently working on similar data compilation projects.
EPA Region 5 is focusing on field sites applying phytoremediation to remediate
radionuclides and EnviroCanada is focusing on total petroleum hydrocarbon (TPH) sites.
Together, the three data sets will address six of the seven major contaminant groups,
leaving only non-halogenated organics to be addressed.

Though plans have not been thoroughly investigated or confirmed, there is a possibility that
the data collected in this project will be incorporated into a searchable software program
for easier use and navigation in the future.
                                                     26

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      PHYTOREMEDIATION FIELD STUDIES DATABASE for
CHLORINATED SOLVENTS. PESTICIDES. EXPLOSIVES, and METALS

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Wilmington, NC

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in
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remediation including excavation and off-site dispo:

Comments








n
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berry Schnoor, University of Iowa (319) 335-5586.
GRACE Bioremediation Technologies, Inc. [DARAT
Bill Rainey, Plexus Scientific brainey@plexsci.com

Primary Contact













'y?
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Multiple Biotechnology Demonstrations of Explosiw
http://aec.army.mil/prod/usaec/et/restor/ecsoils.htm

Citation


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the groundwater by the hybrid poplar trees and/or the microbes
complicated hydrogeological setting and trenching, it is difficult t
balance on perchlorate to prove efficacy of treatment in the field




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between April and November 2003. Irrigation was discontinued
on November 1 7.





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Army Environment Center, Aberdeen Proving G
Sikora, F.L. et al (1 997), "Phytoremediation of e
innovative wetlands-based treatment technologi
Waste Research - Abstracts Book, May 19-22, 1
Best, E.P.H. et al (1 997), Fate and mass balanc
groundwater from Ihe Milan Army Ammunition P
Presentation 1 4. In 1 2th Annual Conference on
Kansas City, MO.




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Ammunition Plant in flow-through
Conference on Hazardous Waste



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soil and phytoavailability under field
Plant and So// article


Citation
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        Appendix E: USDA Soil Classification System
        (adopted from the 1993 USDA Soil Survey Manual)

For most sites, soil particles in the contaminated medium were less than 2 mm, and the
following soil texture classification system was used. Sites containing a contaminated soil
medium of larger particle sizes (i.e. rock fragments) or manufactured soils were described
using language found in the site literature or documentation, or in reference to USDA
manual.

Figure 1. Sand, clay, and silt percentages for soil texture classification
                             •«&,•
Prior to classifying soils, it is important to discuss the three mineral components of soils
that are categorized based on particle size: sands, silts, and clays. Particles that range
from about 0.05 mm to 2 mm in size are sands. Particles between 0.002 mm and 0.05 mm
are classified as silts. Particles less than 0.002 mm are clays. Further breakdown based on
soil textures is as follows:

Sands: Contain more than 85% sand, and the percentage of silt plus 1.5 times the
percentage of clay is less than 15.
    1. Coarse sand: Greater than or equal to 25% or more very coarse and coarse sand;
      less than 50% ay other single grade of sand.
   2. Sand: Greater than or equal to 25% or more very coarse, coarse, and medium
      sand; less than 25% very coarse and coarse sand; less than 50% fine sand and/or
      very fine sand.
   3. Fine sand: 50% or more fine sand; less than 25% very coarse, coarse, and
      medium sand; less than 50% very fine sand
   4.  Very fine sand: 50% or more very fine sand
I
                                   A151

-------
I
Loamy sands: Between 70 and 91% sand and the percentage of silt plus 1.5 times the
percentage of clay is 15 or greater; the percentage of silt plus twice the percentage of clay
is less than 30.
    1.  Loamy coarse sand: Greater than or equal to 25% or more very coarse and coarse
      sand; less tha 50% any other single grade of sand
    2.  Loamy sand: Greater than or equal to 25% or more very coarse, coarse, and
      medium sand; less than 25% very coarse and coarse sand; less than 50% fine
      and/or very fine sand
    3.  Loamy fine sand: Greater than or equal to 50% fine sand; less than 50% very fine
      sand; less than 25% very coarse, coarse, and medium sand
    4.  Loamy very fine sand: 50% or more very fine sand.

Sandy loams: Between 7% and 20% clay,  greater than 52% sand, and the percentage of
silt plus twice the percentage of clay is 30 or more; or, less than 7% clay, less than 50%
silt, and more than 43% sand.
    1.  Coarse sandy loam: Greater than or equal to 25% or more very coarse and coarse
      sand; less than 50% any other single grade of sand
    2.  Sandy loam: Greater than or equal to 30% very coarse, coarse, and medium sand;
      less than 25% very coarse and coarse sand; less than 30% fine and/or very fine
      sand. Or, less than or equal to 15% very coarse, coarse, and medium sand, less
      than 30% fine and/or very fine sand, and less than or equal to 40% fine or very
      fine sand.
    3.  Fine sandy ham: Greater than or equal to 30% fine sand, and less than  30% very
      fine sand. Or, between 15%-30% very coarse, coarse, and medium sand. Or,
      greater than or equal to 40% fine and very fine sand, one half of which  is fine
      sand, and less than  or equal to  15% very coarse, coarse, and medium sand.
    4,   Very fine sandy loam: Greater than  or equal to 30%  or more very fine sand and
      less than 15% very coarse, coarse, and medium sand. Or, greater than 40% fine
      and very fine sand, more than half of which is very fine sand, and less than 15%
      very coarse, coarse, and medium sand.

Loam: Between 7% and 27% clay, 28% and 50% silt, and 52% or less sand.
    1.  Silt loam: Greater than or equal to 50% or more silt and between 12% and 27%
      clay. Or, between 50% and 80% silt and less than 12% clay
    2.  Sill: greater than or equal to 80% or more silt, and less than  12% clay.
    3.  Sandy clay loam: Between 20% and 35% clay, less than 28% silt, and more than
      45% sand.
    4.  Clay ham: Between 27% and 40%  clay and more than 20%-46% sand.
    5.  Silly clay ham: Between 27% and 40% clay and less than or equal to 20% sand.
    6.  Sandy clay: Greater than or equal to 35% clay and greater of equal to than 45%
      sand
    7.  Silty clay: Greater than or equal to 40% clay and greater than or equal to 40% silt.
  4Clay: Greater than or equal to 40% or more clay, less than 45%  sand, and less than
40% silt.
                                                    A152

-------
Appendix F: Climate Table
State
AK
AK
AK
AK
AK
AK
AK
AK
AL
AL
AL
AL
AR
AR
AR
AR
AR
A2
AZ
AZ
AZ
CA
CA
CA
CA
CA
CA
CA
CA
CA
CA
CA
CA
CO
CO
CT
DE
DE
FL
FL
FL
FL
City
Barrow
Bethel
Fairbanks
Gulkana
Juneau
King Salmon
Nome
Sitka Airport
Birmingham
Mobile
Montgomery
Tuscaloosa
Fayetteville (Airport)
Fort Smith
Little Rock
Pine Bluff
Texarkana
Flagstaff
Phoenix
Tuscon
Yuma
Bakersfield
Barstow
Berkeley
Bishop
Blythe
Eureka
Fresno
Los Angeles
Sacramento
San Diego
San Francisco
Santa Barbara
Denver
Grand Junction
Hartford
Dover
Wilmington
Gainesville
Jacksonville
Miami
Orlando (Sanford)
Spring
Frost Date
8/4
6/21
5/25
6/23
5/30
6/8
7/8
5/7
4/14
3/19
3/28
4/8
5/3
4/14
4/8
4/4
3/29
6/26
3/16
3/27
2/19
3/3
4/15
1/19
5/25
3/1
3/14
4/1
2/11
3/23
3/30
1/24
2/26
5/20
6/1
5/12
4/19
4/25
3/29
3/14
none
3/4
Fall Frost
Date
7/24
9/5
8/25
8/9
9/5
8/27
8/17
10/11
10/24
11/5
10/29
10/20
10/4
10/18
10/27
10/26
10/29
9/9
11/18
11/7
12/14
11/20
10/29
12/26
9/26
11/28
11/15
11/7
12/8
11/14
11/12
12/8
12/4
9/20
9/16
9/23
10/15
10/15
11/5
11/16
none
12/3
Elevation
(ft)
26
39
499
1578
23
49
10
66
630
30
200
187
1250
446
259
207
361
7004
1112
2558
207
492
1929
6
4146
262
59
338
148
69
42
7
16
5333
4848
174
36
36
157
30
13
98
Low
Temperature
(F)
-54
-48
-€2
-58
-22
-48
-54
0
-6
3
0
-1
-15
-10
-4
_2
5
-23
19
16
24
19
7
26
-8
20
21
18
30
18
32
24
20
-25
-23
-26
0
-14
10
7
30
19
High
Temperature

-------
*
State
FL
FL
FL
GA
GA
GA
GA
GA
GA
GA
HI
HI
HI
IA
IA
IA
IA
ID
ID
ID
IL
IL
IL
IL
IN
IN
IN
KS
KS
KS
KS
KS
KY
KY
KY
LA
LA
LA
LA
LA
LA
MA
MD
ME
Ml
City
Pensacola
Tallahassee
Tampa
Albany
Atlanta
Augusta
Brunswick
Columbus
Macon
Savannah
Hilo
Honolulu
Lihue
Cedar Rapids
Des Moines
Mason City
Ottumwa
Boise
Idaho Falls
Pocatello
Chicago
Peoria
Rockford
Springfield
Evansville
Ft. Wayne
Indianapolis
Dodge City
Good land
Salina
Topeka
Wichita
Bowling Green
Lexington
Padicah
Alexandria
Baton Rouge
Lafayette
Lake Charles
New Orleans
Shreveport
Boston
Baltimore
Augusta
Detroit
Spring
Frost Date
3/20
4/5
2/25
3/31
4/10
4/15
3/18
4/8
4/4
3/30
none
none
none
5/13
5/9
5/20
5/2
5/26
6/14
6/12
4/25
5/8
5/13
5/1
4/23
5/15
5/9
5/7
5/16
5/4
5/4
5/1
4/28
5/3
4/18
3/26
3/18
3/17
3/18
3/21
4/2
5/3
4/11
5/12
5/12
Fall Frost
Date
11/8
10/28
12/3
10/26
10/25
10/23
11/15
10/27
10/25
10/31
none
none
none
9/25
9/21
9/16
10/5
9/22
9/4
9/6
10/22
10/6
9/25
10/6
10/12
9/25
10/7
10/11
9/23
10/9
10/1
10/10
10/7
10/10
10/15
10/31
11/4
11/6
11/5
11/15
10/27
10/5
10/29
9/22
10/9
Elevation
(ft)
76
69
7
208
977
134
10
387
354
46
30
39
103
902
968
1174
840
2706
4728
4477
658
653
725
617
430
856
807
2593
3680
1275
879
1321
538
1063
397
77
59
36
9
7
174
30
148
354
619
Low
Temperature
(F)
6
6
18
7
-8
-1
13
-2
-6
3
53
52
50
-28
-24
-30
-23
-25
-38
-33
-27
-25
-27
-22
-21
-22
-23
-21
-27
-24
-26
-21
-21
-21
-15
5
-8
9
11
11
3
-7
-7
-19
-13
High
Temperature
(F)
105
103
99
101
105
108
99
104
108
105
94
94
90
104
108
104
105
110
102
104
104
105
104
106
104
106
103
109
108
109
110
112
107
103
105
104
102
102
103
102
107
102
105
97
103
Precipitation
(in)
58.9
65.8
43.9
48.3
50.8
44.6
53
51
44.6
49.2
129.7
22.1
43.1
33.4
33.1
32.7
33.8
12.1
10.9
12.1
35.8
36.2
37.1
35.3
43.1
34.7
39.9
21.5
18.2
30.1
35.2
29.3
51
44.5
48.9
53.1
60.8
58.6
55.3
62.2
46.1
41.5
40.7
42
26.6
                                                A154

-------
State
Ml
Ml
Ml
Ml
MN
MN
MN
MO
MO
MO
MO
MS
MS
MS
MT
MT
MT
MT
NC
NC
NC
NC
ND
NO
ND
ND
NE
NE
NE
NE
NE
NH
NH
NJ
NJ
NJ
NJ
NM
NM
NM
NV
NV
NV
NV
City
Lansing
Marquette
Muskegon
Traverse City
Duluth
International Falls
Minneapolis
Joplin
Kansas City
Springfield
St. Louis
Columbus
Jackson
Meridian
Billings
Bozeman
Butte
Helena
Asheville
Charlotte
Greensboro
Raleigh
3ismark
Dickinson
Fargo
Minot
Grand Island
Lincoln
North Platte
Omaha
Scottsbluff
Concord
Mt. Washington
Atlantic City
Millville
Newark
Trenton
Albuquerque
Gallup
Las Vegas
Ely
Las Vagas
Reno
Winnemucca
Spring
Frost Date
5/31
5/25
5/24
6/9
6/4
6/9
5/21
4/26
4/30
5/2
4/30
4/11
4/7
4/12
5/29
6/19
7/1
6/2
4/24
4/25
4/22
4/29
5/26
6/9
5/25
5/31
5/16
5/9
5/25
5/12
5/25
6/9
7/29
5/15
4/29
4/15
4/15
5/25
6/14
5/29
6/30
4/3
6/19
6/26
Fall Frost
Date
9/18
10/4
9/24
9/17
9/10
9/4
9/15
10/13
10/9
10/8
10/8
10/15
10/14
10/19
9/6
8/31
8/23
9/2
10/11
10/14
10/14
10/16
9/7
8/28
9/12
9/2
9/26
9/30
9/10
9/23
9/14
9/8
8/2
9/28
10/10
10/26
10/23
9/26
9/15
9/22
8/21
11/7
8/23
8/26
Elevation
(ft)
859
1414
644
625
1424
1118
833
987
742
1364
564
200
291
295
3569
4467
5530
3827
2239
787
902
443
1673
2542
895
1722
1853
1181
2788
1027
3854
338
6268
52
72
7
190
5104
6465
6501
6262
2030
4526
4300
Low
Temperature
(F)
-29
-34
-15
-37
-39
-46
-34
-15
-19
-17
-18
-2
2
0
-32
•46
-52
-38
-7
-5
-8
-9
-43
-35
-35
-36
-28
-33
-34
-23
-42
-33
-46
-2
-10
-8
-4
-17
-34
-26
-30
12
-16
-37
High
Temperature
(F)
100
99
99
101
97
98
105
108
110
108
107
104
106
107
105
103
99
105
95
103
103
105
109
109
106
106
110
108
108
110
109
102
72
102
102
105
102
105
99
99
100
117
105
108
Precipitation
(in)
30.6
36
32.6
29.8
30
24.3
28.4
43.2
36.1
43.2
37.5
55
55.4
56.7
15.1
14.7
12.2
11.6
38.8
43.1
42.6
41.4
15.5
16.1
19.5
18.7
24.9
28.8
19.3
29.9
15.3
36.4
98.9
36.7
42.1
43.9
42
8.9
11.3
16.1
10.1
3.4
7.5
8.2
A155

-------
t
State
NY
NY
NY
NY
NY
OH
OH
OH
OH
OH
OH
OH
OK
OK
OR
OR
OR
OR
OR
OR
OR
PA
PA
PA
PA
PA
SC
SC
SC
SC
SO
SD
SD
SD
TN
TN
TN
TN
TX
TX
TX
TX
TX
TX
City
Albany
Buffalo
New York City
Rochester
Syracuse
Akron
Cincinnati
Cleveland
Columbus
Dayton
Toledo
Youngstown
Okalahoma City
Tulsa
Baker City Airport
Eugene
Klamath
Pendleton
Portland
Redmond
Salem
Allen town
Harrisburg
Philadelphia
Pittsburg
Williamsport
Beaufort
Charleston
Columbia
Greenville
Huron
Pierre
Rapid City
Sioux Falls
Chattanooga
Knoxville
Memphis
Nashville
Amarillo
Austin
Brownsville
Dalhart
Dallas/ Ft Worth
El Paso
Spring
Frost Date
5/24
5/20
4/13
5/18
5/14
5/21
4/29
5/18
5/9
4/27
5/16
5/24
4/15
4/13
6/29
5/22
6/28
5/3
4/26
7/17
5/22
5/5
5/4
4/14
5/26
5/16
3/28
4/6
4/17
5/5
5/27
6/2
5/26
5/24
4/18
4/9
4/8
4/16
4/30
3/21
2/15
5/9
4/8
4/14
Fall Frost
Date
9/19
9/23
10/27
9/29
10/3
10/2
10/13
10/5
10/3
10/16
9/29
9/29
10/16
10/21
8/26
10/1
8/31
10/5
10/18
8/20
9/28
10/2
10/4
10/28
9/20
9/30
11/1
10/30
10/16
10/8
9/15
9/8
9/14
9/17
10/19
10/23
10/27
10/14
10/14
11/5
12/17
10/11
10/24
10/28
Elevation
(ft)
292
705
98
544
426
1214
760
804
833
1004
669
1178
1280
676
3372
430
4099
1200
33
3050
180
380
340
27
1223
522
21
49
226
956
1282
1469
3247
1440
689
981
510
600
3615
617
20
3995
574
3913
Low
Temperature
(F)
-28
-20
-2
-19
-26
-24
-15
-19
-19
-24
-20
-20
-8
-8
-39
-7
-25
-19
6
-28
-5
-12
-9
-7
-18
-17
10
6
-1
-6
-39
-33
-23
-36
-10
-24
-14
-17
-12
4
16
-18
-1
-8
High
Temperature
(F)
99
97
104
98
97
101
101
104
101
102
104
100
110
110
106
108
100
113
107
108
108
105
107
104
103
103
104
104
107
103
112
114
109
110
105
102
106
105
108
106
106
107
113
112
Precipitation
(in)
36.1
38.6
47.2
31.9
38.9
36.6
39.7
36.6
38.1
36.6
32.9
37.4
33.3
40.6
10.6
49.4
12.6
12
36.3
8.6
39.2
43.5
40.5
41.5
36.8
40.7
51.2
51.5
49.9
50.6
20.1
18.7
18.6
23.8
53.5
47.1
50.9
47.3
19.5
31.9
26.6
17.5
33.7
8.8
                                              A156

-------
                                             t
State
TX
TX
TX
TX
UT
UT
UT
UT
VA
VA
VA
VT
VT
WA
WA
WA
WA
WA
WA
Wl
Wl
Wl
Wl
Wl
Wl
WV
WV
WY
WY
WY
WY
WY
City
Houston
Midland
San Antonio
Wichita Falls
Cedar City
Logan
Salt Lake City
Wendover
Norfolk
Richmond
Roanoake
Burlington
Montpelier
Bellingham
Olympia
Seattle
Spokane
Walla Walla
Yakima
Eau Claire
Green Bay
Lacrosse
Madison
Milwaukee
Wausau
Charleston
Parkers burg
Casper
Cheyenne
La ramie
3ock Springs
Sheridan
Spring
Frost Date
3/17
4/11
3/23
4/13
6/8
5/22
5/18
5/8
4/6
4/27
4/29
5/25
6/3
5/6
5/17
4/20
5/20
4/19
5/20
5/26
5/26
5/15
5/13
5/20
5/22
5/9
5/9
6/8
6/8
6/26
6/11
6/6
Fall Frost
Date
11/14
10/21
11/6
10/24
9/14
9/27
9/29
10/10
10/31
10/13
10/5
9/19
9/8
10/1
9/30
10/27
9/19
10/20
9/21
9/15
9/18
9/29
9/25
9/26
9/6
10/5
10/2
9/7
9/9
8/26
9/1
9/7
Elevation
(ft)
102
2857
581
1027
5852
4300
4225
4241
26
164
1174
335
1099
59
36
125
1922
1166
1135
892
699
672
872
672
1191
951
840
5320
6143
7186
6370
3952
Low
Temperature
(F)
7
-11
6
-8
-24
-13
-18
-10
-3
-8
-11
-30
-34
-1
-8
9
-25
-24
-17
-39
-29
-36
-30
-26
-36
-15
-20
-41
-29
-50
-37
-37
High
Temperature

-------
 I
t
                                              Appendix G

                                               Resources
                Internet Resources:
                1.     RTDF Phytoremediation Profiles website
                      http://rtdf.org/public/phyto/siteprof/index.cfra

                2.     EPA REACH IT website
                      http://www.epareachit.org/

                3.     CLU-IN Innovative Remediation Technologies: Field Scale Demonstration
                      Project Database and Report
                      http://clu-in.org/products/nairt/

                4.     EPA Superfund Innovative Technology Evaluation (SITE) Project Status
                      Information
                      http://www.epa.gov/ORD/SITE/projectstatus.htm

                5.     Federal Remediation Technologies Roundtable (FRTR)
                      http://www.frtr.gov/

                6.     MIST Chemistry Webbook
                      http://webbook.nist.gov/chemistry/

                Database resources:

                   •  Science Direct
                   •  LexisNexis
                   •  EBSCOhost
                   •  MEDLINE
                   •  BIOSIS
                   •  National Technical Information Service (NT IS)
                   •  Energy Science and Technology
                   •  General Science Abstracts
                   •  Waternet
                   •  Agricola
                   •  CAB Abstracts
                   •  Science.gov
                   •  USDA PLANTS database
                                                    A158

-------
                                                                                               I
                                 Appendix H

                                  References
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Pollutants. Environmental Science and Technology. 34(20): 4259-4265.

Angle, JS; Chancy, RL; Baker, AJM; Li, Y; Reeves, R; Volk, V; Roseberg, R; Brewer, E; Burke,
S; Nelkin, J. 2001. Developing commercial phytoextraction technologies: practical
considerations. South African Journal of Science. 97(11-12): 619-623.

ASTDR. 2004: http://www.atsdr.cdc.gov/toxprofiles/. Updated 7/26/04

Baghour, M; Morenp, DA; Villora, G; Lopez-Cantarero, I; Hernandez, J; Castilla, N; Romero, L.
2002. Root-Zone Temperature Influences on the Distribution of Cu and Zn in Potato-Plant
Organs. Journal of Agricultural and Food Chemistry. 50: 140-146.

Baker, AJM. 1989. Terrestrial Higher Plants which hyperaccumulate metallic elements -
A review of their Distribution, Ecology, and Phytochemistry. Bioreceovery. 1: 81-126
Barraclough, D; Kearney, T; Croxford, A. 2004. Bound residues: environmental solution
or future problem? Environmental Pollution. Article In Press.
Baz, M.; Fernandez, RT. 2002. Evaluating woody ornamentals for use in herbicide
phytoremediation. Journal of the American Society for Horticultural Science. 127(6): 991-997.

Belden, JB; Philips, TA; Coats, JR. 2004. Effect of prairie grass on the dissipation,
movement, and bioavailability of selected herbicides in prepared soil columns.
Environmental Toxicology and Chemistry. 23(1): 125-132.
Bhadra,  R., R.J.  Spanggord, D.G. Wayment, J.B. Hughes, and J.V. Shanks. 1999.
Characterization of oxidation products of TNT metabolism in aquatic phytoremediation systems
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