H200 Plus™

Product Specifications

HEPURE’s new and improved H200 PlusTM product line replaces H200TM which for years has been the industry standard for Insitu Chemical Reduction (ISCR). Since entering the environmental remediation market in 1996, H200™ has been the most widely used micro-scale fine iron powder in the market. Numerous published articles and technical presentations have demonstrated its success at more than 36 sites across North America.

H200 Plus™ represents a significant improvement which we expect will become the new benchmark for ZVI powders.

H200 Plus™ is a proprietary high reactivity zero-valent iron material available exclusively through HEPURESM. It is designed to provide superior, cost-effective performance for most in-situ applications. The specific distribution of iron particles in H200 Plus™ ensures high initial reactivity combined with a longer reactive life to optimize and maintain reducing conditions in the treatment zone. It has effectively been used to remediate halogenated organic compounds, heavy metals and toxic metalloid contaminants. Typical iron content is 95.5%. H200 Plus™ can be provided with customized grain-size distribution to meet site-specific conditions.

Contact HEPURESM for references on H200 Plus™ Plus applications.

Typical Powder Characteristics

Trace Elements
ppm (wgt.)
Li = 32 Cr = 25 Sn = 4
Be = 0.28 Co = 180 Hg = <0.1
B = 6.5 Cu = 12 Bi = <0.01
Na = 45 Ga = 100 Pd = <0.1
Al = 1500 As = 8 Ag = 1.2
Ca = 500 Zr = 7.6 Cd = <0.1
Ti = 1000 Mo = 5 Mg = 1800
V = 1500 Ge = 15 Si = 400
Mn = 800 Se = <0.05 Sc = 4.5
Ni = 230 Nb = <0.5 Sb = 1.3
Zn = 4 In = <0.1 Pb = <0.05
Chemical Analysis
wt%  
Carbon 0.25
Sulfur 0.01
Oxygen 1.2
Hydrogen Loss 1.0
Physical Properties
Aparent Density, g/cu.cm 2.55
Surface Area, sq.m/g 0.1
Particle Size
sieve analysis, wt%
>100 mesh Trace
>140 4
>200 25
>230 16
>325 25
Pan 28
Laser Diffraction
Micrometre
D10 45
D50 85
D90 140
 
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Manufacturing Process

In the sponge iron process, high purity magnetite iron ore is reduced to pure iron in a high temperature, solid-state reduction process.

The reduction takes place in a tunnel kiln, and has many similarities to ceramic processes, upon which the sponge iron process was developed. Because of the solid-state nature of the reduction process, sponge iron powders are irregular in shape, and characterized by a high degree of interconnected porosity. The high surface area associated with sponge iron renders them uniquely suited for chemical applications.


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Treated Contaminants

H200 is effective in treating a wide range of chlorinated compounds or heavy metals. Don't see your compound? Contact Us and we will tell you if it can be treated by H200.

tick Tetrachloroethene (PCE) tick Carbon Tetrachloride (CT)
tick Trichloroethene (TCE) tick Trichloromethane (TCM)
tick cis 1,2-Dichloroethene (cDCE) tick Tribromomethane (TBM)
tick trans 1,2-Dichloroethene (tDCE) tick 1,2-Dibromoethane (12EDB)
tick 1,1-Dichloroethene (11DCE) tick Trichlorotrifluoroethane (Freon 113)
tick Vinyl Chloride (VC) tick Trichlorofluoromethane (Freon 11)
tick Hexachloroethane (HCA) tick 1,2,3-Trichloropropane (123TCP)
tick 1,1,2,2-Tetrachloroethane (1122TeCA) tick 1,2-Dichloropropane (12DCP)
tick 1,1,1,2-Tetrachloroethane (1112TeCA) tick Lindane
tick 1,1,1-Trichloroethane (111TCA) tick Hexachlorobutadiene (HCBD)
tick 1,1,2-Trichloroethane (112TCA) tick N-nitrosodimethylamine (NDMA)
tick 1,1-Dichloroethane (11DCA)    

Materials & Safety Data Sheet

H-200 Materials Safety Data Sheet can be downloaded here in the following format:

 
Download H-200 MSDS in PDF format (123kb)

Frequently Asked Questions

Q: What is the difference between sponge, atomized powder and cast iron?
A:  Sponge powder is produced from magnetite iron ore that is directly reduced at elevated temperatures. The material is then disintegrated into powder. Sponge iron has a very high surface area and exhibits high green strength. To produce atomized powders, molten steel is atomized into irregular and homogeneous particles which are then annealed.

Q: What are the standard packaging sizes?
A:  Standard packaging sizes are as follows:

  • 50 lb. bags
  • 500 lb. fiber drums
  • 2205 lb. flexible bags
  • 5000 lb. bulk packs

Laboratory Data

Feroxsm Chromium (Cr +6) Treatment (Lab.)

Completed bench-top treatability tests on the reduction of hexavalent chromium in groundwater and soils using H200 ZVI powder were performed. The goal of the study was to derive field design parameters and dosage levels to reduce (Cr +6) contamination to its less toxic and insoluble tri-valent (Cr+3) state. As shown in the photo, groundwater and soil from the site had an initial lime-green color due to the high concentrations of (Cr +6). The studies evaluated several dosages of H200 powder in reducing the Cr +6 to Cr+3 within 30 days. As the Cr+3 precipitates out, the groundwater is treated. As shown, the color of the groundwater changed from lime-green to clear as Cr +6 was reduced.

Benchscale Research Study of Feroxsm Treatment of Marine Sediment - Trenton, NJ

Project Summary
In conjunction with Stevens Institute of Technology, research was performed to evaluate the effectiveness of Zero Valent Iron in treating contaminated sediment from NY/NJ harbor. Sediment for the study was selected from an area that serves as a tributary to the East River in New York. The sediment was found to consist primarily of silts and clays, and contained a high organic content. Furthermore, a chemical baseline analysis of the sediment revealed the presence of polychlorinated biphenyls (PCBs), chlorinated pesticides and toxic leachable metals.

The two year study demonstrated the feasibility of zero valent iron in treating many toxic compounds commonly found in dredge sediment.


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H-200 Powder out performs other Iron Powders
Reactivity Data (click to enlarge)

The H-200 ZVI powder used in the Feroxsm process is a proprietary high reactive zero valent iron powder exclusively available through Hepuresm. Directly reduced from iron ore and manufactured in the USA, this material contains no toxic levels of trace elements. The H-200 is codex “food-grade” certifiable due to its high purity and the manner in which it is produced. Internal porosities on the individual iron particles, along with other inclusions found within its structural matrix (not as a separate phase), result in enhanced reactivity for the particle.

Hepure also observed during this test the use of H-200 generated little or no daughter products such as cis-1,2-DCE and vinyl chloride compared to the other commercial irons. This confirms the field data from numerous project sites in which the TCE was degraded preferentially by the beta-elimination process without creating the daughter products rather than by sequential dechlorination.

The test also showed that the reactivity of a iron powder is not dictated by particle size or surface area. As part of product R&D, Hepure had previously tested other types of very fine powder that showed lower reactivities.

H200 Treatment on DNAPL

A Treatability Study was performed to evaluate the use of Zero-Valent Iron (ZVI) to treat groundwater and soils impacted with TCE at concentrations that would suggest the presence of DNAPL existing in saturated and unsaturated zones beneath a government site in Alabama. The presence of DNAPL level concentrations were identified within the upper ground water transition zone at the site. A treatability test was performed to determine the use of varying ratios of zero-valent iron to treat soils and groundwater impacted with TCE, cis-1,2-DCE, 1,1,2-trichloro-1,2,2-trifluoroethane (Freon-113) and trichlorofluoromethane (Freon-11) within a DNAPL environment.

Until recently, ZVI has typically been used to treat dissolved phase and residual contamination present in the saturated zone. The utilization of ZVI to treat very high contamination levels under partially saturated conditions was not addressed; therefore, the purposes of the treatability tests were to:

  • Evaluate the feasibility of using ZVI to remediate contaminated soils and groundwater impacted with DNAPL phase levels of TCE and Freon-113.
  • Evaluate the effective dosages of zero-valent iron, which will be required in the field to reflect the results obtained during this Study.
  • Confirm that no undesirable by-products associated with the reduction of the target contaminants will result from the field application of the process.
    Summary of Treatability Study Findings
  • Baseline analysis of site groundwater indicated elevated concentrations of TCE and Freon-113. The highest TCE concentrations (362,000 mg/l), were detected in well CW03-082. Freon-113 concentrations in CW03-082 were 12,000 mg/l, while concentrations of cis-1,2-dichlorothene were 2400 mg/l. VC was not detected in the groundwater samples.
  • Baseline analysis of site soils collected from a depth of 15 – 29 feet bgs indicated elevated concentrations of TCE and Freon-113 indicative of DNAPL conditions. The highest TCE concentrations were reported at a depth of 15.5 feet bgs, corresponding to a TCE concentration of 290,400 mg/kg.
  • The laboratory treatability study resulted in the a 99% reduction of elevated levels of TCE (5370 mg), in a groundwater-soil slurry created from samples collected from the site. TCE reductions exceeding 99% were achieved with all the iron ratios evaluated following 52 days of treatment.
  • Slower kinetic rates were observed using the lowest iron ratio of 0.2 grams. A 99% reduction was achieved with the 0.2 grams following 52 days of treatment. In addition, higher quantities of cis-1,2-DCE were detected following the completion of the study, corresponding to a mass of 55.5 mg.
  • In the pH range encountered in our studies where the initial pH ranged from 5.0 –7.0, the influence of pH on the rate constants were inconclusive. This may be attributed to the slightly acidic conditions, which provide sufficient H+ ions for the reaction to occur. In addition, the presence of the H+ ions may act to mask the influence of pH changes on the kinetic rate.
  • An evaluation of the 1 gram, 2 gram and 5 gram iron ratios, demonstrated that ZVI can reduced both TCE and Freon-113 simultaneously, without the formation of elevated levels of cis-1,2-DCE, and VC. This was observed following 52 days of treatment, in which levels of cis-1,2-DCE were found to be low (<4 mg). The accumulation of other daughter products (particularly VC) was not detected.
  • The presence of sulfate and nitrate did not have an impact on the targeted CVOC reduction. Sulfate reductions by ZVI were found to be inconclusive. Nitrate was reduced by the iron for all the ratios with the exception of 5 grams. The presence of nitrate within the 5 gram ratio following 52 days was due to effects of pH.
  • As shown in Figures 5, 6 and 7, the reduction of TCE follows an approximate first-order kinetics at the tested iron-to-TCE ratios. The study also demonstrated the dependence of iron ratio of the reaction kinetics, where higher ratios resulted in a more rapid rate of TCE reduction. In addition, the higher iron ratios were more effective at controlling the accumulation of daughter products associated with the reduction of TCE.



In summary, the data from this test demonstrated the Hepure ZVI's ability to treat high concentration-level organic chemicals.

The Reductive De-chlorination of Chlorinated Compounds Using Iron Powder

Presented at the I&EC Special Symposium
American Chemical Society
Pittsburgh, PA
September 15-17, 1997
H. Ito, T. Kimura - DOWA Mining Company, Ltd.
J.J. Liskowitz - Hepure Technologies, Inc.

INTRODUCTION
In recent years, chlorinated volatile organic compounds (CVOC's) such as trichloroethylene (TCE), tetrachloroethylene (PCE), or 1,1,1-trichloroethane (MC) have caused serious contamination to soils and groundwater. Several treatment methods against this problem have been considered and one innovative approach is reductive degradation using zero-valence iron. Previous works showed the reduction of 14 kinds of chlorinated solvents with iron powder (IP)1 and the kinetics of the reduction for carbon tetrachloride (CT) with IP2. In our laboratory a process for treatment of industrial waste water for heavy metals or COD by IP (DOWA IRON POWDER Method) has been developed and commercialized as a laboratory treatment equipment3. In this study it was concluded that chlorinated solvents, such as TCE, PCE, or MC, could be degraded by IP in aqueous solution. Furthermore, the degradation of TCE and PCE with IP could be enhanced with reductants which show weak acidity, like sodium hydrogen sulfite (NaSO3).

Experimental Section
Chemicals. The chemicals used were TCE, PCE, MC, 1,1,2-trichloroethane (1,1,2-TCA), sodium hydrogen sulfite, sodium sulfite (Wako Pure Chemical Industries, Ltd., Japan), 1,1-dichloroethene (1,1-DCE), cis-1,2-dichloroethene (c-DCE), vinyl chloride (VC), and 1,1,2,2-tetrachloroethane (TeCA) (GL-Sciences Inc., Japan). IPs used here were E-200, DE, DNC-240 (DOWA Iron Powder Co., Ltd., Japan) for the reduced iron, and cast iron powder (Wako Pure Chemical Industries, Ltd., Japan). DE was pre-reduced one for DNC-240 through the manufacturing process. Surface area for each IP, determined by BET analysis, was 2.2 m2/gram for E-200, 0.5 m2/gram for DE, and 0.1 m2/gram for DNC-240.

Model Reaction Systems. All CVOC's reaction experiments were carried out in 120-ml glass hypovials as batches at 25oC. Appropriate amounts of IP (no treatment) and 100 ml of de-ionized water were added to hypovials. The hypovials were then crimp-sealed immediately with aluminum caps with Teflon-lined septa. CVOCs were taken with glass syringe and injected into the hypovials through the septa to be 100 mg/l. Then 20 ml of head space was left. The reactions were then started with mixing by a shaker at 120 min-1. To measure the concentrations for CVOCs and their intermediates, 100 micro-l of the head space gas was taken by gas-tight syringe and injected into a gas chromatograph with flame ionization detector (FID). At the same time, 2-micro-l of benzene was added to each hypovial as an internal standard.

RESULTS AND DISCUSSION
The Degradation of TCE and PCE Using IP.

Figure 1 shows the time course for 100 mg/l of TCE (7.6 x 10-4 M) mixed with various amounts of E-200 (0, 1200, 6000, 12000 mg/l). The concentration of TCE was decreased exponentially in accordance with the amount of IP. So the reaction was expected to follow pseudo first-order process described below;

ln C / Co = -k1t

k1 = k2 [Fe]

More than 80 mol% of TCE was degraded by 12000 mg/l of IP after two weeks. And the chlorine, which were to be displaced from TCE, existed in the aqueous solution as Cl- ion (97% of the yield). However, Table 1 shows that k2 values do not correspond to the amount of IP and they decreased constantly with it. This might be caused from that mixing of IP in those systems was not complete enough to show a homogenous reaction.

PCE was also degraded by IP, whose k1 value was about one eighth times as large as that of TCE.

It was clear that TCE or PCE could be degraded by IP in aqueous solution, however approximately 20 intermediates were also detected in the systems simultaneously through the degradation. So more details for the TCE or PCE degradation pathways have to be considered.

The Effects of Reductants Such as Hydrogen Sulfite Ion. It is generally known that about 8 mg/l of oxygen exists in water as dissolved oxygen (DO) at room temperature. DO was thought to oxidize IP to ferric oxide and inhibit degradation of CVOCs. In order to remove DO from the systems, reductants (deoxygenating agents) were mixed into the system. And also, in our previous work it was obvious that controls of pH in the system could effect the reduction by IP on its surface significantly. The effects of the reductants which showed weak acidity (NaHSO3) or weak basicity (Na2SO3). It appeared that the k1 values showed remarkable increases along with NaHSO3 concentration. On the other hand, Na2SO3 showed less increase compared to NaHSO3.

Enhanced degradation of TCE and PCE night have arisen from the IP surface that was more reductive by NaHSO3. Other reductants which showed weak acidity like sodium pyrosulfite (NaS2O5) or sodium hydrosulfite (Na2S2O4) in aqueous solution were confirmed to increase CVOCs' degradation rates as well as NaHSO3.

TABLE 2: The comparison of k1 and k1-r among four kinds of IP.

Table 2 shows the k1 (without NaHSO3 in the system) and k1-r (with 2000 mg/l NaHSO3) values degrading PCE using four kinds of IP. Thought these values varied with the IPs, NaHSO3 was expected to increase k1 values in any cases except for DNC-240 (see the last column of k1-r / k1). Furthermore, significant differences of k1 values were shown clearly with each IP.

Application to other CVOCs. As described above, chlorinated ethenes like TCE and PCE were degraded by IP in aqueous solution. In our laboratory applications to other types of CVOC degradation, such as chlorinated methanes, ethanes or aromatics using IP were also conducted. As a result, chlorinated ethanes like MC, 1,1,2-TCA, TeCA could be degraded via de-hydrochlorination with IP. Chlorinated methanes or aromatics, however, could not be degraded by IP in the same condition.

CONCLUSIONS
Based on the investigations, the following conclusions were made:

1. Chlorinated ethenes like TCE and PCE were degraded by IP in the aqueous solution. The degradation might follow a pseudo first-order process with respect to the amount of IP through second-order rate constants, k2, could not correspond to each amount of IP.

2. TCE or PCE degradation rates using IP were highly increased adding weak acid reductancts such as NaHSO3 to the systems, where weak base reductants could not increase the rates in the same conditions.

3. Degradation rates, k1, varied with the different sorts of IP. From the results, E-200 was found to be the most reactive of the four IPs used in this test.

4. Applications of IP to other CVOCs like chlorinated ethanes, methanes, or aromatics were investigated and chlorinated ethanes such as 1,1,2-TCA or TeCA could be degraded via de-hydrochlorination with IP.

Further analysis of the intermediates for the degradation of CVOCs is under investigation and then the degradation mechanisms can be considered in more detail.

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This article was reprinted from the original with permission from the authors. No portion of this article may be used without written permission from the authors

Experimental Evaluation of Biotic & Abiotic Treatment of Energetic Compounds


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