Design Tool - Base Addition for ERD

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Acids are produced during Enhanced Reductive Dechlorination (ERD) which can cause pH to drop, inhibiting treatment. Alkaline materials including hydroxides and carbonates are sometimes added to the aquifer during ERD to maintain a pH of greater than 6, improving bioremediation performance. This article describes a simplified approach and a spreadsheet-based design tool for estimating the total amount of base required to achieve a specified target pH at the end of the treatment period, once all reactions have gone to completion. To prevent overshoot and excessively high pH, users typically add a fraction of the total base required in several increments spread over time.

Related Article(s):

Contributor(s): Dr. Robert Borden, P.E.

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Aquifer pH lower than 6 can reduce the efficiency of enhanced reductive dechlorination (ERD) and other in situ remediation processes. This article describes a simplified approach using a spreadsheet-based design tool for estimating the total amount of base required to achieve a specified target pH at the end of the treatment period, once all reactions have gone to completion. This approach requires simplification of several important processes controlling subsurface pH, and is only appropriate for developing initial estimates of the total amount of base required. In practice, aquifer pH should be monitored during ERD and periodically adjusted to maintain conditions for optimal microbial growth and contaminant degradation. Early in the bioremediation process, reactions will not have gone to completion and less base will be required to maintain the target pH. To prevent overshoot and excessively high pH, users typically add a fraction of the total base required in several increments spread over time.

Background Aquifer pH

In humid areas, rainfall combined with carbonic acid produced in the soil leaches out base cations (Na+, K+, Ca2+, Mg2+) gradually acidifying the soil. Figure 1 shows soil pH in the contiguous United States.

Figure 1. Soil pH in the contiguous US (Soil pH). Alkaline soils (pH>7.4) are shown in blue. Acidic soils (pH<6.1) are shown in brown.

Groundwater pH is influenced by soil pH, but also by other factors. As acidic water infiltrates through the soil profile, some of the acidity may be neutralized by dissolution of soil and aquifer minerals. Silicate minerals including feldspars and micas can hydrolyze over time, consuming acid, and releasing dissolved cations (Na+, K+, Ca2+, Mg2+). However, these weathering reactions are slow, and are often not sufficient to prevent pH declines during ERD. Figure 2 shows a cumulative frequency distribution of groundwater pH at a site in eastern North Carolina. Average soil pH at this site is approximately 5. The vadose zone and surficial aquifer at the site are predominantly quartz sand and weathered clays, so weathering processes provide minimal buffering capacity. 90% of the groundwater pH measurements were between 4.5 and 6.0 indicating low soil pH at this site was a reasonable predictor of acidic groundwater. At other sites containing carbonate minerals or relatively young rocks, mineral dissolution often results in greater buffering.

Figure 2. Cumulative frequency distribution of groundwater pH measurements at site in eastern North Carolina where soil pH is approximately 5.

Groundwater Acidity

Acidity is the amount of base required to neutralize acids present in a water sample. Since various acids can disassociate to different extents, two solutions with the same pH can have different acidities (see pH Buffering in Aquifers). In most cases, the acidity of the background groundwater is the sum of acidity from strong mineral acids (phosphoric, nitric, sulfuric, and hydrochloric acids), organic acids, and dissolved carbon dioxide. Mineral acidity (also referred to as methyl orange acidity) is determined by titrating a sample with a strong base to pH=3.7 (Standard Method 2310, AWPA 2016). If the initial pH is greater than 3.7, mineral acidity is zero. The spreadsheet-based design tool presented here uses this measurement to account for the base demand of any strong acids already present in the aquifer. Total acidity (commonly referred to as phenolphthalein acidity) should not be used to calculate the amount of base required because the titration endpoint of this parameter is pH 8.3, which will over-estimate the base requirement for optimal ERD.

Under low pH conditions, organic volatile fatty acids (acetic, propionic, etc.) can accumulate and contribute to acidity. However, in background groundwater, organic acid concentrations are generally low. In the design tool, acidity from background organic acids is assumed to be negligible.

In theory, acidity from dissolved carbon dioxide can be measured using a modification of Standard Method 2310[2] in which the sample is titrated to a target pH using a strong base. When using this approach, special precautions should be taken to prevent any pH shift due to degassing of dissolved carbon dioxide from the sample during transport to the laboratory or during analysis of the sample. In the design tool, acidity from background dissolved carbon dioxide is instead calculated from the dissolved inorganic carbon concentration (DIC) and background pH. This eliminates the problem of pH shift due to dissolved carbon dioxide degassing. Commercial laboratories can measure DIC using a modification of the Total Organic Carbon (TOC) procedure.

Aquifer Buffering Capacity

An aquifer’s buffering capacity is the resistance to pH change and is primarily due to two processes: (1) buffering by dissolved and solid carbonates; and (2) surface complexation and/or ion exchange reactions on mineral surfaces. While mineral weathering processes do influence long-term pH changes, weathering reactions are often too slow to prevent pH declines due to HCl and CO2 production during ERD.

Figure 3. Distribution of H2CO3*, HCO3- and CO32- as a function of pH.

Buffering by Dissolved and Solid Carbonates In natural aqueous systems, pH buffers are predominantly weak acid anions that easily bind and release hydrogen ions. The most common are the weak acid anions produced by dissolved CO2 [3][4]. When CO2 dissolves in water, some CO2 combines with H2O forming carbonic acid (H2CO3). For convenience, the sum of dissolved CO2 and H2CO3 is often written as H2CO3*. H2CO3*can then disassociate releasing a bicarbonate ion (HCO3-) and one H+ or a carbonate ion (CO32-) and two H+ by the following reactions[5]:

H2CO3* ⇔ H+ + HCO3- ⇔ 2 H+ + CO32-         Reactions 1 and 2

Figure 3 shows the relative distribution of these solutes as a function of pH. The reactions are reversible so that (a) an influx of acid will cause the HCO3- and CO32- ions to protonate, consuming the acid, or (b) an influx of base will cause dissociation (deprotonation) of H2CO3* and the bicarbonate ion to consume the base. The maximum resistance to pH change (buffering capacity) occurs when the pH is equal to the dissociation constant of either carbonic acid (pH = 6.3 @ 25°C) or of the bicarbonate ion (pH = 10.3 @ 25°C). The buffering capacity of groundwater is measured with an alkalinity titration[6][2]. The units of alkalinity can be given as milliequivalents (meq) per liter, but are often reported as mg CaCO3/L (milligrams of CaCO3 per liter) using the following equation:

Alkalinity (mg CaCO3/L) = Alkalinity (meq/L) × 50 (mg CaCO3/meq)                Equation 1

For a system open to a large reservoir of carbon dioxide (e.g. the atmosphere), the buffering capacity (assuming no soluble minerals are present) is a function of the partial pressure of carbon dioxide in the reservoir. Near the water table, groundwater is open to the atmosphere and can release excess dissolved CO2 gas if its partial pressure is greater than the reservoir’s, essentially stripping some acid out of the groundwater by partially reversing the above reactions.

In a closed system (e.g. below the water table), the buffering capacity is a function of the total dissolved carbonates (H2CO3*, HCO3-, and CO3-2). When solid carbonate minerals are present (CaCO3, MgCO3, CaMg(CO3)2, FeCO3), carbonate mineral dissolution can limit pH declines caused by strong acids (e.g. HCl). For example, in an aquifer containing solid CaCO3, the ambient groundwater is saturated with CaCO3 (s). When HCl is produced by ERD, groundwater pH declines, and dissolved CO32- also declines as the carbonate ion is protonated by the added H+ ions causing an increase in HCO3- and/or H2CO3* (see Figure 3). The groundwater is now under-saturated and CaCO3 will dissolve, consuming H+ by the following reaction:

CaCO3(s) + H+ ⇒ Ca2+ + HCO3-                 Reaction 3
Figure 4. Buffering capacity of aquifer solids from SA-17 and OU-2 measured in DI water[1]. The legend shows depth below ground surface in feet for individual samples.

However, the solubility of carbonate minerals is relatively low, so solid carbonates are much less effective in limiting pH declines due to CO2 production in the saturated zone. Below the water table, CO2 may not degas, causing a buildup of HCO3-. Geochemical modeling[7] indicates that the aquifer can become supersaturated with CaCO3 during ERD, causing carbonate dissolution to stop. As additional CO2 is produced, CaCO3 (s) will precipitate producing H+ by the following reaction:

H2CO3* + Ca2+ + CO32- ⇒ H+ + HCO3- + CaCO3(s)                 Reaction 4

Surface Complexation and Ion Exchange Reactions H+ sorption to Fe and Al oxyhydroxides and clay minerals through surface complexation and ion exchange reactions can have a major impact on pH. H+ adsorbs strongly to some mineral surfaces, which can accumulate large amounts of H+ as the solution pH declines and release the H+ back to solution as the pH rises[8][9]. This strong buffer can reduce the pH decline in many systems, but can also greatly increase the amount of base required to increase aquifer pH.

Estimating Aquifer Buffering Capacity

Figure 5. Aquifer buffering capacity (pHBC) from multiple ERD sites[1].

When carbonate minerals are present, geochemical models[7] are needed to determine the amount of buffering provided by carbonate mineral dissolution. However, in many naturally low pH aquifers, carbonate minerals are absent and the extent of buffering can be estimated by adding a strong base to the aquifer solids, equilibrating for several days, and measuring the resulting pH. These buffering curves are typically linear in the pH range of 4.5 to 6.5[10][11][12] recommend carrying out the titrations in a uniform ionic strength solution, most commonly 0.01 M CaCl2.

Figure 4 shows the measured final pH versus meq of OH- added per kg of dry aquifer material. Incremental base addition results in a nearly linear increase in pH. The slopes of these curves were estimated by linear regression. pH buffer capacity (pHBC) is calculated as the inverse of the slope and is reported in units of milliequivalents per kilogram (meq/kg) per pH unit.

Figure 5 shows cumulative frequency distributions for pHBC in 6 different contaminated aquifers in the eastern U.S. Within a single unit, pHBC values are reasonably constant, with the middle 50% of measurements varying by a factor of two. However, median pHBC values can vary by a factor of ten between sites and even between sandy versus clayey units on the same site.

Acid and Base Production

Multiple processes can produce or consume acidity during ERD including redox, precipitation, and hydrolysis reactions. Table 1 shows the amount of H+ released from some important redox reactions.

Table 1. Net Acid Production from Important Redox Reactions
e- Acceptor e- Donor Product Reaction H+ Produced
per mole e- donor
PCE H2 TCE C2Cl4 + H2 → C2H3Cl3 + H+ + Cl- 1
TCE H2 cDCE C2HCl3 + H2 → C2H2Cl2 + H+ + Cl- 1
cDCE H2 VC C2H2Cl2 + H2 → C2H3Cl + H+ + Cl- 1
VC H2 Ethene C2H3Cl + H2 → C2H4 + H+ + Cl- 1
H2O Acetic Acid H2, HCO3- C2H4O2 + 4 H2O → 2 H2CO3* + 4 H2 2 (1 - α)
H2O Lactic Acid H2, HCO3- C3H6O3 + 3 H2O → 3 H2CO3* + 6 H2 3 (1 - α)
H2O Glucose H2, HCO3- C6H12O6 + 12 H2O → 6 H2CO3* + 12 H2 6 (1 - α)
H2O Soybean Oil H2, HCO3- C56H100O6 + 162 H2O → 56 H2CO3* + 156 H2 56 (1 - α)
Oxygen H2 H2O O2 + 2 H2 → 2 H2O 0
Nitrate H2 N2, OH- NO3- + 2 ½ H2 → 2 H2O + ½ N2 + OH- -1
Goethite H2 Fe2+, OH- FeO(OH) + ½ H2 → Fe2+ + 2 OH- -2
Sulfate H2 HS- SO42- + 4 H2 + Fe2+ → FeS + 4 H2O 0
H2CO3* H2 CH4 H2CO3* + 4 H2 → CH4 + 2 H2O α - 1

During reductive dechlorination of PCE (C2Cl4) to TCE (C2HCl3), a chlorine atom (Cl) is replaced with hydrogen (H2) releasing one proton (H+) and one chloride (Cl-).

C2Cl4 + H2 ⇒ C2HCl3 + H+ + Cl-                Reaction 5

As TCE is further dechlorinated to cDCE, VC and ethene, an additional proton is released for each chlorine removed. As a result, ERD can release large amounts of acid. For example, complete reduction of one kilogram of PCE to ethene produces 0.9 kilograms of HCl.

Organic substrates added as electron donors ferment in oxygen-poor environments, releasing H2 and acetic acid. Acetic acid rarely accumulates during ERD, because it can be used by various cohorts of organisms for reduction of PCE and TCE, for reduction of background electron acceptors, or for fermentation to methane (CH4). Consumption of acetic acid by all of these processes produces H2CO3*. The amount of H2CO3* produced during fermentation of different substrates can be estimated with the following formula:

CθHβOγ + (3θ - γ) H2O ⇒ θ H2CO3* + (2θ + β/2 - γ) H2                Reaction 6
θ is the number of carbon atoms per mole of substrate
β is the number of hydrogen atoms per mole of substrate
γ is the number of oxygen atoms per mole of substrate

Figure 6. Fraction of H2CO3* not ionized (α) versus pH.

As shown in Figure 3, CO32- is only present in significant concentrations at pH > 8. For pH ranges relevant for ERD (5>pH>8), H+ release from H2CO3* can be represented by the following reaction[5].

H2CO3* ⇒ α H2CO3* + (1 - α) H+ + (1 - α) HCO3-                 Reaction 7

where α is the fraction of H2CO3* that does NOT ionize at the target pH with α = (1+ 10-6.352 / [H+])-1. Figure 6 shows the variation in α as a function of pH. At pH 6, α = 0.69, so 0.31 moles of H+ are released for every mole of CO2 produced. However at pH 7, α = 0.18, so 0.82 moles of H+ are released for every mole of CO2 produced.

Reduction of some electron acceptors produces OH-, counter-acting acid produced from dechlorination and CO2 production. Representative reactions for reduction of nitrate (NO3-), iron oxides, sulfate (SO42-) and bicarbonate (HCO3-) are included in Table 1. Goethite [FeO(OH)] is used as a typical iron oxide for these calculations.

Base Addition

A variety of different bases have been used to raise the aquifer pH to stimulate ERD including soluble and solid carbonates, soluble and solid hydroxides, phosphates and silicate minerals. The carbonates and hydroxides are used most commonly because of their relatively low cost and easy availability. Table 2 summarizes the physical properties of common basic salts used to raise pH.

Table 2. Physical Properties of Common Basic Salts used for pH Control
Base Formula Molecular
(eq/kg Base)
solution pH
Caustic Soda NaOH 40.0 1 25.0 1,100 >14
Caustic Potash KOH 56.1 1 17.8 1,200 >14
Soda Ash Na2CO3 106 1 + α 11.2 300 ~11.7
Baking Soda NaHCO3 84 α 2.2 78 ~8.3
Hydrated Lime Ca(OH)2 74.1 2 27.0 1.85 ~12.4
Mg(OH)2 58.3 2 34.3 <0.01 ~10.3

NaOH and KOH provide a large number of OH- equivalents (eq) per kg and are very soluble so only small volumes of base are required to raise the aquifer pH. However, concentrated solutions of NaOH and KOH have pH > 14 which is inhibitory to bacteria, would expose workers to safety hazards, and can partially dissolve aluminosilicates.

As described above, solid calcium carbonate (CaCO3) is generally not effective in raising pH during ERD because of its low aqueous solubility. Na2CO3 and NaHCO3 are much more soluble and can be effective in raising aquifer pH. The amount of H+ consumed per mole varies as a function of pH between pH 5 and 8[5]. For closed conditions (below water table where CO2 cannot degas) and pH < 8, NaHCO3 and Na2CO3 disassociate to H2CO3* and HCO3-, consuming H+ by the following reactions.

NaHCO3 + α H+ ⇒ Na+ + α H2CO3* + (1 – α) HCO3-                 Reaction 8
Na2CO3 + (1 + α) H+ ⇒ 2 Na+ + α H2CO3* + (1 – α) HCO3-                 Reaction 9

At pH = 6, α = 0.69 so 0.69 moles of H+ are consumed per mole of NaHCO3 and 1.69 moles of H+ consumed per mole of Na2CO3 (Figure 6). However at pH = 7, α = 0.18 so only 0.18 moles of H+ are consumed per mole of NaHCO3 and 1.18 moles of H+ consumed per mole of Na2CO3. As a result, bicarbonates and carbonates are relatively effective at raising the pH to 6. However, these materials provide less alkalinity per unit mass at pH =7, increasing the amount of material required.

Ca(OH)2 and Mg(OH)2 provide large amounts of OH- per kg. However, these materials have a low aqueous solubility, making them more difficult to distribute in the subsurface.[13] describe the use of a colloidal form of Mg(OH)2 with improved transport properties.

Design Tool

An MS Excel based design tool was developed to aid in estimating the amount of base required to achieve a specified target pH at the end of the treatment period, once all reactions have gone to completion[1]. The general approach and calculations were presented in the previous sections. The design tool is specifically focused on pH adjustment for ERD and calculation procedures include the following assumptions.

  1. The target pH is between 5 and 8.
  2. The carbonate system is the primary aqueous pH buffer.
  3. Organic acids including volatile fatty acids (acetic, propionic, etc.) are consumed and do not accumulate.
  4. Any H2 or acetate produced by substrate fermentation that is not consumed through reduction of chlorinated solvents and background electron acceptors (O2, NO3, iron oxides, and SO4) is consumed by methanogenesis.
  5. All processes and reactions have gone to completion. The calculated total base requirement is for the end of the treatment period once all acids (HCl and H2CO3) have been produced.

In general, the most important factors controlling base requirement are: a) initial and target pH; b) amount of substrate consumed; c) aquifer buffering capacity (pHBC); and d) amount of iron oxides reduced. To calculate base requirement, design tool users must enter the following information.

  1. Treatment zone dimensions and design period for this phase of remediation.
  2. Site characteristics including average hydraulic conductivity (K), porosity, hydraulic gradient, contaminant concentrations in aquifer material and groundwater, and amount of electron acceptors to be produced (i.e. CH4) or consumed (O2, NO3, Fe, SO4).
  3. Background pH, total inorganic carbon, mineral acidity, and pH buffering capacity (pHBC). A database of pHBC measurements is provided to aid users in selecting design values when laboratory measurements are not available.
  4. Mass of organic substrate and base to be injected.
  5. When vegetable oil is used as a substrate, the fraction of injected oil that is consumed during the design period.
  6. Target pH

Users are reminded that the design tool calculates the total amount of base required once all reactions go to completion. Early in the bioremediation process, reactions will not have gone to completion and less base will be required to maintain the target pH. To prevent overshoot and excessively high pH, users typically add a fraction of the total base required in several increments spread over time.

Figure 7. Required base addition for PRB for different target pH values.

Case Study

The design tool was used to estimate the amount of base required to stimulate ERD in a 435 ft long emulsified vegetable oil (EVO) biobarrier at Operable Unit 2 (OU2) on the former Naval Training Center (NTC) in Orlando, FL[1]. The biobarrier consists of two rows of injection wells spaced approximately 30 ft on center which were treated with a total of 20,224 lb of vegetable oil. The vertical treatment thickness was 10 ft, influent groundwater pH ~5, and pHBC = 8 meq/kg/pH. To provide guidance on amounts of base required, the design tool was used to estimate the amount of NaOH, Na2CO3, NaHCO3, or Mg(OH) 2 required to achieve different pH values at the end of the five year treatment period. Results presented in Figure 7 indicate that the amount of base required is very sensitive to the target pH. For target pH values < 5.4, little or no base is required. Increasing the target pH to 6 or 7, requires progressively greater amounts of base because of the soil acidity and carbonic acid released from substrate fermentation.

To achieve a pH of approximately 7, 10,200 lb of NaOH or 7,400 lb of Mg(OH)2 are required, which is equivalent to 50% or 37% respectively (by weight) of the vegetable oil injected. Multiple NaOH injections would be required since a single injection would result in an excessively high initial pH and the base would migrate out of the treatment zone over time with flowing groundwater. The total mass of Mg(OH)2 required is less than NaOH, since two moles of OH- are released per mole of Mg(OH)2. However, Mg(OH)2 has a very low aqueous solubility, so the material must be injected in a colloidal form. Since the material is a solid and would not migrate downgradient, 100% of the required Mg(OH)2 could be injected simultaneously with the EVO. The pH of a pure slurry of Mg(OH)2 is relatively high (~10.3). However once injected, CO32- precipitates on the surface of the Mg(OH)2 particles forming a MgCO3 coating that maintains the aquifer pH between 7 and 8[14]. In general, it is not practical to raise the pH to near 7 with NaHCO3 due to the small amount of H+ consumed by this material at near neutral pH. Na2CO3 could be effective, but would require multiple injections due to the high pH (~11.7) and downgradient migration with groundwater flow.


Alkaline materials are commonly added during ERD to maintain an aquifer pH of greater than 6. A simplified approach and spreadsheet-based design tool are presented for estimating the total amount of base required to achieve a specified target pH at the end of the treatment period, once all reactions have gone to completion. To prevent overshoot and excessively high pH, users typically add a fraction of the total base required in several increments spread over time. Users should be aware that results are very sensitive to variations in the target pH since the amount of H+ released from carbon dioxide and consumed by NaHCO3 and Na2CO3 is a function of pH.


  1. ^ 1.0 1.1 1.2 1.3 1.4 Borden, R.C., 2017. Post-Remediation Evaluation of EVO Treatment: How Can We Improve Performance. Environmental Security Technology Certification Program, Alexandria, VA. ER-201581Report.pdf
  2. ^ 2.0 2.1 American Public Health Association, American Water Works Association and Water Environment Federation (APWA, AWWA, and WEF), 2016. Standard Method 2320 Alkalinity, Standard methods for the examination of water and wastewater. Report.pdf
  3. ^ Langmuir, D., 1997, Aqueous Environmental Geochemistry. Prentice-Hall, Inc. Upper Saddle River, NJ ISBN: 978-0023674129.
  4. ^ Drever, J.I., The Geochemistry of Natural Waters: Surface and Groundwater Environments. Prentice-Hall, Inc., ISBN 0132727900.
  5. ^ 5.0 5.1 5.2 Stumm, W. and Morgan, J.J., 1996. Aquatic chemistry; an introduction emphasizing chemical equilibria in natural waters. ISBN-13: 978-0471091738 and ISBN-10: 0471091731
  6. ^ U.S. Geological Survey, 2015. National field manual for the collection of water-quality field data, Alkalinity and acid neutralizing capacity. US Geological Survey Techniques of Water-Resources Investigations, book 9, chap. A6., sec. 6.6. [[media:USGS-2015-Natl_Field_Manual.pdf| Report pdf]
  7. ^ 7.0 7.1 Robinson, C., Barry, D.A., McCarty, P.L., Gerhard, J.I. and Kouznetsova, I., 2009. pH control for enhanced reductive bioremediation of chlorinated solvent source zones. Science of the Total Environment, 407(16), pp.4560-4573. doi:10.1016/j.scitotenv.2009.03.029
  8. ^ Davis, J.A. and Kent, D.B., 1990. Surface complexation modeling in aqueous geochemistry. Reviews in Mineralogy and Geochemistry, 23(1), pp.177-260. doi: 10.1021/es980312q
  9. ^ Davis, J.A., Coston, J.A., Kent, D.B. and Fuller, C.C., 1998. Application of the surface complexation concept to complex mineral assemblages. Environmental Science & Technology, 32(19), pp.2820-2828. doi: 10.1021/es980312q
  10. ^ Magdoff, F.R. and Bartlett, R.J., 1985. Soil pH Buffering Revisited 1. Soil Science Society of America Journal, 49(1), pp.145-148. doi: 10.2136/sssaj1985.03615995004900010029x
  11. ^ Liu, M., Kissel, D.E., Cabrera, M.L. and Vendrell, P.F., 2005. Soil lime requirement by direct titration with a single addition of calcium hydroxide. Soil Science Society of America Journal, 69(2), pp.522-530. doi:10.2136/sssaj2005.0522
  12. ^ Aitken, R.L. and Moody, P.W., 1994. The effect of valence and ionic-strength on the measurement of pH buffer capacity. Soil Research, 32(5), pp.975-984. doi: 10.1071/SR9940975
  13. ^ Borden, R.C., Lai, Y.S., Overmeyer, J., Yuncu, B. and Allen, J.P., 2016. In situ pH adjustment with colloidal Mg(OH)2. Environmental Engineer and Scientist: Applied Research and Practice, accepted for publication, Vol 17, pp.28-33.
  14. ^ Hiortdahl, K.M. and Borden, R.C., 2013. Enhanced reductive dechlorination of tetrachloroethene dense nonaqueous phase liquid with EVO and Mg (OH)2. Environmental science & technology, 48(1), pp.624-631. doi: 10.1021/es4042379

See Also