Metals Treatment and Removal Mechanisms
1
Metals Treatment and Removal Mechanisms Neutral Mine Drainage Treatment with Constructed Wetlands Mark W. Fitch, Joel G. Burken, Chang Ye Department of Civil, Architectural and Environmental Engineering; University of Missouri-Rolla, Rolla, Missouri Disturbance Testing: Release of Metals Rationale: Various forms have differing stability and are stability is environmentally dependent. When environmental parameters such as pH or redox change, different forms may not remain sequestered. Some of these environmental changes such as reconstruction work, bioturbation by rooting animals, or drying from drought conditions or drainage can be abrupt and could potentially result in a high concentration, short duration release of the sequestered metals. The uncertainty of the effects of disturbances on the fates of fixed metals in constructed wetlands could stifle application. Testing: Wetland media was taken from the 6 year old wetland, separated and placed into two new wetlands, similar to Figure 1. The two were subjected to different tests; 1. Physical disturbance (i.e. repeated mixing) and 2. Drying. Following the perturbations, influent was returned and the effluent was tested for both filtered and unfiltered Pb and Zn levels. Findings: Effluent metals concentrations in the physical disturbance test were elevated in the unfiltered samples, Figure 6. The particulate form of the metals suggests that sequestered metals were not chemically altered, but rather the release of colloidal sized particulates, as is likely as colloidal lead sulfides and lead-DOM complexes have been identified, Figures 4 & 5. The release was very brief and repeated mixing did not result in continued release, showing that the sequestered metals were stable. Effluent from the drying test was elevated in dissolved metals, reaching up to 450 ppb. The release was quite brief as in just a few pore volumes, the lead levels dropped back below the average influent concentration, Figure 7. The brief duration of the impacts suggest that wetlands are robust in their functionality and can quickly recover after anticipated perturbations. Acknowledgements This work was funded by the Midwest HSRC (National Center for Environmental Research STAR Program, EPA) and Doe Run Mining Company. The authors acknowledge Bill Duncan, Teck Cominco Mining, Trail BC, Canada for data and support. We also thank Cem Selman, Rebecca Leerssen, Ying Song, and Chad Ross for assistance. Abstract: Heavy metals at low levels in mine drainage, mine tailings leachate, and industrial wastewater is a national issue. In Missouri, the legacy of lead mining during the last 130 years includes several Superfund sites. Constructed wetlands pose a passive treatment system that may provide efficient, sustainable treatment for long periods at such sites. Laboratory scale wetlands have been operating for 6 years, sustaining effective lead and zinc removal and reducing toxicity to acceptable levels. Removal mechanisms include: sorption to the wetlands media, precipitation as metal sulfides, and co-precipitation with iron oxy/hydroxides. Any of the three mechanisms can dominate under different design and operating conditions. Tests on the wetland media following years of metals accumulation show that small fractions of the metals can be remobilized under certain conditions. Physical disturbance of the media resulted in elevated metals being released in a colloidal fraction, whereas a drying period resulted in an increase in the soluble metals, likely do to oxidation of metals sulfides. Findings overall show that constructed wetlands can efficiently and effectively treat alkaline mine drainage and process waters, and design and operations are important in optimizing treatment and long-term stability. Conclusions & Recommendations • Constructed wetlands can provide sustained removal of Pb and Zn and reduce whole effluent toxicity (WET) with minimal operations and maintenance. • Metals’ sequestration occurs via three primary mechanisms: Adsorption, Sulfide precipitation & Iron oxy/hydroxide coprecipitation. Multiple, complimentary mechanisms result in the observed reliability. • Adsorption capacity is higher than previously thought, related to wetlands’ composition. • Sulfide precipitation was observed, but was slower than thought and appears to be of lesser importance than previously published. • Remobilization is a minimal concern after the wetlands have sequestered the metals and can be mitigated by avoiding dry conditions and major disturbances of Figure 1 Schematic of laboratory wetlands Objectives: • Investigate the relative fates of Pb and Zn in constructed wetlands.. • Elucidate removal capacity and failure modes of constructed wetlands treating Pb and Zn. • Determine the impact of disturbances on the sequestered metals. • Develop design and operational information on wetlands treatment of mine drainage and process waters. Plexiglas screen Effluent Glass aquarium Gravel Influent Substrate 12” 6” 18” 26” 3” 12” Aerated Tap Water Mixer Chemicals Overview: Treatment wetlands were prepared in the laboratory, Figure 1. Media used in the wetland were partially based on local availability and low cost and included: chip bark, alfalfa, composted manure, silica sand, and peat moss. Removal has averaged 90% for Pb and 75% for Zn overall and been steady over 6 years. Individual removal mechanisms were investigated in laboratory experiments, including sulfide generation and precipitation of metal-sulfide precipitates, adsorption isotherm determinations and sequential extraction and microscopic analyses of media from operating wetlands. Adsorption: Greater sorption potential than previously thought was discovered. Individually, wetland components had higher sorption capacities than had been shown, Figure 2. Recent kinetics testing suggests that sorption may be more rapid, reaching apparent equilibrium in as little as 12 hours. Sulfide Precipitation: Sulfide generation and metal-sulfide precipitation potential was tested using a dialysis membrane to isolate media and surface phenomenon. Sulfide was actively generated by the wetland media, and lead was repeatedly removed from solution, Figure 3. Sulfate reducing bacteria (SRB) were identified in the laboratory wetlands. Using Scanning Electron Microscope-Energy Diffraction Spectrometry (SEM-EDS) zinc sulfide and lead sulfide, Figure 4, were positively identified in wetland media. Iron Coprecipitation: Lead and zinc rapidly coprecipitated with iron oxy/hydroxides. Iron oxides were clearly present in the laboratory wetlands. Sequential extraction showed that up to 30 to 70% of Pb and Zn were removed in the gravel lens and the initial portion of the wetland media. Coprecipitation was highly variable on iron content and aeration time. Summary: Overall, removal of zinc and lead was consistent over 6 years in laboratory wetlands. The effluent had a negligible toxicity to fathead minnows and C. dubia. Estimates on relative fates were generated, Figure 5. One remaining question is the potential precipitation of metals following desorption from the wetland media if the local metals concentration is decreased in the presence of sulfide. Kinetics suggest that sorption is much more rapid, yet sulfides were readily located. 0 1 2 3 4 0 24 48 72 96 Tim e (hour) P b (ppm ) 0 days 17 days 35 dys 64 days 103 days control S 2- PbS Dialysi s Tubing Wetland Media Figure 3 Sulfide precipitation 0 200 400 600 800 1000 1200 0 50 100 150 200 250 300 350 400 Pb C oncentration (ug/L) A dsorbed Pb (ug/g M oss B ark H ay S and S ubstrate M anure Figure 2 Sorption to wetland media constituent 0 100 200 300 400 500 0 10 20 30 40 50 Volum e (L) Pb (ug/L) Filtered Sam ple U nfiltered Sam ple 0 10 20 30 40 50 0.01 0.1 1 10 100 1000 Volum e (L) Pb (ug/L) Wetland substrate MS M-DOM S -2 M +2 SO 4 -2 (DOM) Gravel lens M 2+ Fe +2 M - Fe m OH n Influent Effluent M-DOM M +2 M adsorb ed ? M- Particle s MCO 3 10-15% reversibly 40-100 ppb 1-5% 1-5% 5-10% 20-40% 30-70% SRB 53% S 47% Pb Figure 4 Lead-sulfide Via SEM - EDS Figure 5 Composite of metals’ fate in lab scale wetlands Figure 6 Effluent from physical disturbance test. Closed symbols are unfiltered samples, open symbols are filtered Figure 7 Effluent from drying test for filtered and unfiltered samples
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Effluent. Influent. Glass aquarium. S 2 -. Aerated Tap Water. 18”. Substrate. 12”. 12”. Dialysis Tubing. Mixer. 3”. 6”. 26”. PbS. Gravel. Chemicals. Plexiglas screen. Wetland Media. Acknowledgements - PowerPoint PPT Presentation
Transcript of Metals Treatment and Removal Mechanisms
Metals Treatment and Removal Mechanisms
Neutral Mine Drainage Treatment with Constructed WetlandsMark W. Fitch, Joel G. Burken, Chang Ye
Department of Civil, Architectural and Environmental Engineering; University of Missouri-Rolla, Rolla, Missouri
Disturbance Testing: Release of MetalsRationale: Various forms have differing stability and are stability is environmentally dependent. When environmental parameters such as pH or redox change, different forms may not remain sequestered. Some of these environmental changes such as reconstruction work, bioturbation by rooting animals, or drying from drought conditions or drainage can be abrupt and could potentially result in a high concentration, short duration release of the sequestered metals. The uncertainty of the effects of disturbances on the fates of fixed metals in constructed wetlands could stifle application.
Testing: Wetland media was taken from the 6 year old wetland, separated and placed into two new wetlands, similar to Figure 1. The two were subjected to different tests; 1. Physical disturbance (i.e. repeated mixing) and 2. Drying. Following the perturbations, influent was returned and the effluent was tested for both filtered and unfiltered Pb and Zn levels.
Findings: Effluent metals concentrations in the physical disturbance test were elevated in the unfiltered samples, Figure 6. The particulate form of the metals suggests that sequestered metals were not chemically altered, but rather the release of colloidal sized particulates, as is likely as colloidal lead sulfides and lead-DOM complexes have been identified, Figures 4 & 5. The release was very brief and repeated mixing did not result in continued release, showing that the sequestered metals were stable. Effluent from the drying test was elevated in dissolved metals, reaching up to 450 ppb. The release was quite brief as in just a few pore volumes, the lead levels dropped back below the average influent concentration, Figure 7. The brief duration of the impacts suggest that wetlands are robust in their functionality and can quickly recover after anticipated perturbations.
AcknowledgementsThis work was funded by the Midwest HSRC (National Center for Environmental Research STAR Program, EPA) and Doe
Run Mining Company. The authors acknowledge Bill Duncan, Teck Cominco Mining, Trail BC, Canada for data and support. We also thank Cem Selman, Rebecca Leerssen, Ying Song, and Chad Ross for assistance.
Abstract: Heavy metals at low levels in mine drainage, mine tailings leachate, and industrial wastewater is a national issue. In Missouri, the legacy of lead mining during the last 130 years includes several Superfund sites. Constructed wetlands pose a passive treatment system that may provide efficient, sustainable treatment for long periods at such sites. Laboratory scale wetlands have been operating for 6 years, sustaining effective lead and zinc removal and reducing toxicity to acceptable levels. Removal mechanisms include: sorption to the wetlands media, precipitation as metal sulfides, and co-precipitation with iron oxy/hydroxides. Any of the three mechanisms can dominate under different design and operating conditions. Tests on the wetland media following years of metals accumulation show that small fractions of the metals can be remobilized under certain conditions. Physical disturbance of the media resulted in elevated metals being released in a colloidal fraction, whereas a drying period resulted in an increase in the soluble metals, likely do to oxidation of metals sulfides. Findings overall show that constructed wetlands can efficiently and effectively treat alkaline mine drainage and process waters, and design and operations are important in optimizing treatment and long-term stability.
Conclusions & Recommendations • Constructed wetlands can provide sustained removal of Pb and Zn and reduce whole effluent toxicity (WET)
with minimal operations and maintenance.
• Metals’ sequestration occurs via three primary mechanisms: Adsorption, Sulfide precipitation & Iron oxy/hydroxide coprecipitation. Multiple, complimentary mechanisms result in the observed reliability.
• Adsorption capacity is higher than previously thought, related to wetlands’ composition.
• Sulfide precipitation was observed, but was slower than thought and appears to be of lesser importance than previously published.
• Remobilization is a minimal concern after the wetlands have sequestered the metals and can be mitigated by avoiding dry conditions and major disturbances of the wetland.
Figure 1 Schematic of laboratory wetlands
Objectives:
• Investigate the relative fates of Pb and Zn in constructed wetlands..
• Elucidate removal capacity and failure modes of constructed wetlands treating Pb and Zn.
• Determine the impact of disturbances on the sequestered metals.
• Develop design and operational information on wetlands treatment of mine drainage and process waters.
Plexiglas screen
EffluentGlass aquarium
Gravel
Influent
Substrate
12”
6”
18”
26” 3”
12”
Aerated Tap Water
Mixer
Chemicals
Overview: Treatment wetlands were prepared in the laboratory, Figure 1. Media used in the wetland were partially based on local availability and low cost and included: chip bark, alfalfa, composted manure, silica sand, and peat moss. Removal has averaged 90% for Pb and 75% for Zn overall and been steady over 6 years. Individual removal mechanisms were investigated in laboratory experiments, including sulfide generation and precipitation of metal-sulfide precipitates, adsorption isotherm determinations and sequential extraction and microscopic analyses of media from operating wetlands.
Adsorption: Greater sorption potential than previously thought was discovered. Individually, wetland components had higher sorption capacities than had been shown, Figure 2. Recent kinetics testing suggests that sorption may be more rapid, reaching apparent equilibrium in as little as 12 hours.
Sulfide Precipitation: Sulfide generation and metal-sulfide precipitation potential was tested using a dialysis membrane to isolate media and surface phenomenon. Sulfide was actively generated by the wetland media, and lead was repeatedly removed from solution, Figure 3. Sulfate reducing bacteria (SRB) were identified in the laboratory wetlands. Using Scanning Electron Microscope-Energy Diffraction Spectrometry (SEM-EDS) zinc sulfide and lead sulfide, Figure 4, were positively identified in wetland media.
Iron Coprecipitation: Lead and zinc rapidly coprecipitated with iron oxy/hydroxides. Iron oxides were clearly present in the laboratory wetlands. Sequential extraction showed that up to 30 to 70% of Pb and Zn were removed in the gravel lens and the initial portion of the wetland media. Coprecipitation was highly variable on iron content and aeration time.
Summary: Overall, removal of zinc and lead was consistent over 6 years in laboratory wetlands. The effluent had a negligible toxicity to fathead minnows and C. dubia. Estimates on relative fates were generated, Figure 5. One remaining question is the potential precipitation of metals following desorption from the wetland media if the local metals concentration is decreased in the presence of sulfide. Kinetics suggest that sorption is much more rapid, yet sulfides were readily located.
0
1
2
3
4
0 24 48 72 96
Time (hour)
Pb
(p
pm
)
0 days17 days35 dys64 days103 dayscontrol
S2-
PbS
Dialysis Tubing
Wetland Media
Figure 3 Sulfide precipitation
0
200
400
600
800
1000
1200
0 50 100 150 200 250 300 350 400
Pb Concentration (ug/L)
Ad
sorb
ed P
b (
ug
/g)
Moss Bark Hay
Sand Substrate Manure
Figure 2 Sorption to wetland media constituents
0
100
200
300
400
500
0 10 20 30 40 50Volume (L)
Pb
(ug/
L)
Filtered Sample
Unfiltered Sample
0
10
20
30
40
50
0.01 0.1 1 10 100 1000Volume (L)
Pb
(ug/
L)
Wetland substrate
MS
M-DOM
S-2
M+2
SO4-2
(DOM)
Gravel lens
M2+
Fe+2 M - FemOHn
Influent
Effluent
M-DOM
M+2
M
adsorbed
?M-Particles
MCO3
10-15%
reversibly
40-100 ppb
1-5%
1-5%
5-10%
20-40%
30-70%
SRB
53% S47% Pb
Figure 4 Lead-sulfide Via SEM - EDSFigure 5 Composite of metals’ fate in lab scale wetlands
Figure 6 Effluent from physical disturbance test. Closed symbols are unfiltered samples, open symbols are filtered
Figure 7 Effluent from drying test for filtered and unfiltered samples
