Abstract:
A method for the reduction and prevention of mercury emissions into the environment from combusted fossil fuels or off-gases having mercury with the use of hypoiodite is disclosed. The hypoiodite is used for the capture of mercury from the resulting flue gases using a flue gas desulfurization system or scrubber. The method uses hypoiodite in conjunction with a scrubber to capture mercury and lower its emission and/or re-emission with stack gases. The method allows the use of coal as a cleaner and environmentally friendlier fuel source as well as capturing mercury from other processing systems.

Description:
TECHNICAL FIELD 
       [0001]    This invention relates to the reduction of mercury emissions into the environment from the combustion of coal and/or other carbon-based fuels as well as from other processing systems. The invention relates to the method of capturing mercury from flue gases by flue gas desulfurization systems or scrubbers thereby reducing the levels of toxic mercury, which enables the use of coal as a clean and environmentally friendlier fuel source as well as makes other processing systems more environmentally desirable. 
       BACKGROUND 
       [0002]    The demand for electricity continues to grow globally. In order to keep stride with the growing demand, coal continues to be a primary source for electricity generation. The burning of coal in power generation plants results in the release of energy, as well as the production of solid waste such as bottom and fly ash, and flue gas emissions into the environment. Emissions Standards, as articulated in The Clean Air Act Amendments of 1990 as established by the U.S. Environmental Protection Agency (EPA), requires the assessment of hazardous air pollutants from utility power plants. 
         [0003]    Conventional coal-fired combustion furnaces and similar devices produce emissions that include pollutants such as mercury. Mercury vapor can contribute to health concerns. At the levels common in the atmosphere, the concentrations of mercury are usually safe. However, mercury can accumulate in ecosystems, for example, as a result of rainfall. Some conventional systems attempt to control mercury emissions with particulate collection devices. 
         [0004]    The primary gas emissions are criteria pollutants (e.g., sulfur dioxide, nitrogen dioxides, particulate material, and carbon monoxide). Secondary emissions depend on the type of coal or fuel being combusted but include as examples mercury, selenium, arsenic, and boron. Coal-fired utility boilers are known to be a major source of anthropogenic mercury emissions in the United States. In December of 2000, the EPA announced its intention to regulate mercury emissions from coal-fired utility boilers despite the fact that a proven best available technology (BAT) did not exist to capture or control the levels of mercury released by the combustion of coal. This has been further complicated by the lack of quick, reliable, continuous monitoring methods for mercury. 
         [0005]    Mercury (elemental symbol Hg) is a metal that melts at 234K (−38° F.) and boils at 630K (674° F.). As such, it can be expected to have a high vapor pressure relative to many metals. The oxidized forms of mercury, Hg 2+  and Hg + , have much lower vapor pressures and can be captured by fly ash particulates. 
         [0006]    Mercury is found in coals at concentrations ranging from 0.02 to 1 ppm. The mercury is present as sulfides or is associated with organic matter. Upon combustion the mercury is released and emitted into the flue gas as gaseous elemental mercury and other mercury compounds. The mercury appears in the flue gas in both the solid and gas phases (particulate-bound mercury and vapor-phase mercury, respectively). The so-called solid-phase mercury is really vapor-phase mercury adsorbed onto the surface of ash and/or carbon particles. The solid-phase mercury can be captured by existing particle control devices (PCDs) such as electrostatic precipitators (ESPs) and fabric filters (FF), the latter sometimes referred to as baghouses. 
         [0007]    Several control strategies have been developed for the control of mercury emissions from coal-fired boilers. Some of these methods include injection of activated carbon, modified activated carbon, various chemical catalysts, and inorganic sorbents. Unfortunately, none of these strategies removes all the mercury from the flue gas. The efficiencies range from as low as 30% to as high as 80% based on the amount of mercury entering the system with the coal. In addition, these technologies either produce unwanted effects on by-products such as impacting the quality of fly ash, or they generate additional waste streams for the power plant. Both lead to higher operational costs for the power plant. One promising strategy is to take advantage of existing air pollution control devices (APCDs) to augment or to serve as the primary means to remove vapor-phase mercury. Two examples of APCDs are semi-dry and wet scrubbers or flue gas desulfurizer (FGD). Semi-dry FGDs are also known as spray dryer absorbers (i.e., SDAs), circulating dry scrubbers (CDS), or TURBBOSORP® available from Von Roll. 
         [0008]    Sulfur oxides (SO x ) regulatory compliance mandates the use of at least one of several control strategies. Three such strategies that are used in the US are sorbent injection into the flue gas following by a particulate collection device such as an ESP or a FF, and wet or dry flue gas desulfurizers. At present, about 3% of the coal-fired power plants are using sorbent injection. FGD scrubbing accounts for 85% using wet and 12% using dry scrubber technologies. Wet scrubbers achieve greater than 90% SO x  removal efficiency compared to 80% by dry scrubbing. In wet scrubbers, the flue gas is brought into contact with slurry containing an alkaline source such as lime or limestone. The SO x  is adsorbed into the water and reacts to form calcium sulfite. It has been demonstrated that simultaneous to SO x  capture, wet FGDs can be used to capture vapor-phase mercury from the flue gas. 
         [0009]    Elemental mercury is water-insoluble and is not removed by a wet FGD. In contrast, oxidized mercury in the flue gas is water-soluble and is removed. The Information Collection Request (ICR) mercury data demonstrated that ionic mercury is removed effectively approaching 90% by wet FGDs. Hence, one strategy for mercury capture is to oxidize all the mercury during the burning of the coal and capture the oxidized mercury in the wet scrubber. Work carried out by URS in conjunction with the Department of Energy/National Energy Technology Laboratory (DOE/NETL) investigated just such a strategy. There are two critical technical steps to the implementation of this strategy. The first is the complete oxidation of the vapor-phase mercury exiting the boiler and the coal. URS, among others, is developing strategies and technologies to accomplish this step. To date, they have demonstrated that independent of the coal type, vapor-phase mercury speciation can be shifted to extensively 100% oxidized mercury. The second critical technical step in the implementation of this control strategy is the sorption of the oxidized mercury and removal in the wet scrubber. The problem, identified early on, is that there are reactions occurring in the wet scrubber liquor that reduce oxidized mercury to elemental mercury and lead to “re-emission” or release of elemental mercury into the scrubbed flue gas. The prevention of ionic mercury reduction in wet scrubber liquor has been studied and reported by G. M. Blythe and D. W. DeBerry at URS and others. 
         [0010]    The findings have suggested that complexation of the ionic mercury is one way to reduce or eliminate the generation of elemental mercury in the scrubber. This same study has demonstrated that not all chelants of ionic mercury can accomplish this in a wet FGD. In a recent presentation, plant results of such a chelant, TMT-15, trimercapto-s-triazine, available from Degussa, were inconclusive regarding the prevention of re-emission of mercury across a wet scrubber. Efficient and cost-effective apparatuses and methods for controlling emissions of mercury remain a desirable need in the art whether from combustion sources such as coal plants and cement kilns or other sources such as incinerators used in a variety of activities. 
       SUMMARY 
       [0011]    In one aspect, a method for reducing mercury emissions is disclosed. In one embodiment, the method includes providing a gas stream comprising mercury and passing the gas stream into a scrubber comprising a scrubber liquor and hypoiodite. 
         [0012]    In one embodiment, the method includes burning a carbonaceous fuel comprising mercury, thereby producing a flue gas, and passing the flue gas into a flue gas scrubber comprising a scrubber liquor and hypoiodite. 
         [0013]    In some embodiments, the hypoiodite is mixed with a carrying agent selected from: limestone slurry, lime slurry, sodium-based alkali solution, trona-based solution, sodium carbonate solution, sodium hydroxide solution, and water. 
         [0014]    In some embodiments, the method also includes mixing an iodine salt and an oxidant to form the hypoiodite. In some embodiments, the oxidant is sodium hypochlorite. 
         [0015]    In some embodiments, the mercury is from combusted coal. In some embodiments, the mercury is from an incinerator. In some embodiments, the mercury is from a cement kiln. In some embodiments, the mercury is from an ore refinery. In some embodiments, the mineral ore processed at the refinery contains phosphorus (such as phosphate). In some embodiments, the mineral ore processed at the refinery contains gold. 
         [0016]    In some embodiments, the scrubber is a wet scrubber selected from spray tower system, a jet bubblers system, and a co-current packed tower system. In some embodiments, the hypoiodite is added to the liquor and then added to the scrubber. In some embodiments, the hypoiodite is added to the scrubber containing the liquor. In some embodiments, the hypoiodite is added to a virgin liquor then added to the scrubber. In some embodiments, the hypoiodite is added to a make-up liquor then added to the scrubber. In some embodiments, the hypoiodite is added to a return liquor then added to the scrubber. In some embodiments, the hypoiodite is added to a reclaimed liquor then added to the scrubber. In some embodiments, the hypoiodite is added to a liquor injected directly into flue gases then added to the scrubber. In some embodiments, the hypoiodite is added to a recirculation loop of the scrubber liquor. In some embodiments, the hypoiodite is added to a low solids return to the scrubber from a scrubber purge stream. In some embodiments, the hypoiodite is added to an aqueous stream introduced into the scrubber. In some embodiments, the hypoiodite is added to a demister. In some embodiments, the hypoiodite is added to a make-up water stream. 
         [0017]    In some embodiments, the mercury is from an incinerator. In some embodiments, the mercury is from a cement kiln. 
     
    
     
       BRIEF DESCRIPTION OF THE DRAWINGS 
         [0018]      FIG. 1  shows a schematic of an experimental setup of impingers to measure simulated mercury emission capture. 
           [0019]      FIG. 2  is a plot that shows the percent of mercury removal as a function of sodium hypochlorite concentration with and without hypoiodite using an embodiment of the invention. 
       
    
    
     DETAILED DESCRIPTION 
       [0020]    Unless expressly stated to the contrary, use of the term “a” is intended to include “at least one” or “one or more.” For example, “a device” is intended to include “at least one device” or “one or more devices.” 
         [0021]    Any ranges given either in absolute terms or in approximate terms are intended to encompass both, and any definitions used herein are intended to be clarifying and not limiting. Notwithstanding that the numerical ranges and parameters setting forth the broad scope of the invention are approximations, the numerical values set forth in the specific examples are reported as precisely as possible. Any numerical value, however, inherently contains certain errors necessarily resulting from the standard deviation found in their respective testing measurements. Moreover, all ranges disclosed herein are to be understood to encompass any and all subranges (including all fractional and whole values) subsumed therein. 
         [0022]    One of skill in the art would also understand that salts of iodine refer to iodine ions typically seen as I −  but which can also exist in a different oxidation state. hypoiodite is an ion known as IO −  which is oxidized more than bromide (Br—). 
         [0023]    The present disclosure describes the use of hypoiodite to unexpectedly improve the capture of mercury emissions across a wet flue gas desulfurizer (FGD) in coal-fired flue gas streams or other processing system where mercury vapor is present or released. Examples include municipal solid waste (MSW) incinerators, medical waste combustors, ore roaster and refineries, and cement kilns. 
         [0024]    The scrubbers currently used in the industry include spray towers, jet bubblers, and co-current packed towers as examples. These types of air pollution control devices (APCDs) are provided as examples and are not meant to represent or suggest any limitation. The hypoiodite may be added to virgin limestone or lime slurry prior to addition to the scrubber, the recirculation loop of the scrubber liquor, the “low solids” return to the scrubber from the scrubber purge stream, demister water, make-up water, or the scrubber liquor. Semi-dry FGDs can also be adapted, including spray dryer absorbers (i.e., SDAs), circulating dry scrubbers (CDS) or TURBBOSORP® available from Von Roll. The hypoiodite may be added to semi-dry FGDs so that the hypoiodite contacts mercury passing through the scrubber. 
         [0025]    Typically, the hypoiodite is applied at a ratio of 0.5:1 to 20000000:1 weight hypoiodite to weight of mercury being captured. The preferred ratio is from 1:1 to 2000000:1 and the most preferred range is from 5:1 to 200000:1. In some embodiments, the hypoiodite is prepared by mixing an iodine salt, for example, potassium iodide (KI) with an oxidant source. The oxidant source may be any oxidant that converts an iodide ion (I − ) to hypoiodite (I—O − ) such as hypochlorite, e.g. sodium hypochlorite. 
         [0026]    In general, hypoiodite may be introduced into the scrubber and thereby into the scrubber liquor via several routes. The following will serve as just some of the variations that are available to introduce the hypoiodite into the scrubber liquor. The scrubber liquor is defined as the water-based dispersion of calcium carbonate (limestone) or calcium oxide (lime) used in a wet or dry flue gas scrubber to capture SO x  emissions. The liquor may also contain other additives such as magnesium and low-molecular weight organic acids, which function to improve sulfur capture. One example of such an additive is a mixture of low-molecular weight organic acids known as dibasic acid (DBA). DBA typically consists of a blend of adipic, succinic, and glutaric acids. Each of these organic acids can also be used individually. In addition, another low-molecular weight organic acid that can be used to improve sulfur capture in a wet scrubber is formic acid. Finally, the scrubber liquor will also contain byproducts of the interaction between the lime or limestone and flue gas, which leads to the presence of various amounts of calcium sulfite or calcium sulfate as well as anions such as halides (i.e., chlorides, bromides, and iodides) and other cations such as iron, zinc, sodium, or copper. The scrubber liquor includes but is not limited to the make-up liquor, return liquor, the reclaimed liquor, virgin liquor, and liquor injected directly into flue gases. 
         [0027]    Another addition point for the hypoiodite to the wet scrubber is at the “low solids” liquor return. A portion of the liquor is often continuously removed from the scrubber for separating reaction byproducts from unused lime or limestone. One such means of separation is centrifugation. In this process, the scrubber liquor is separated into a “high solids” and “low solids” stream. The high solids stream is diverted to wastewater processing. The low solids fraction returns to the wet scrubber and can be considered reclaimed dilute liquor. The hypoiodite may be added to the reclaimed low solids stream prior to returning to the scrubber. 
         [0028]    Another feed liquor found in the operation of a wet FGD is called “virgin liquor.” Virgin liquor is the water-based dispersion of either lime or limestone prior to exposure to flue gas and is used to add fresh lime or limestone while maintaining the scrubber liquor level and efficiency of the wet FGD. This is prepared by dispersing the lime or limestone in water. Here, the hypoiodite can be added either to the dispersion water or to the virgin liquor directly or to the demister water. 
         [0029]    Finally, some scrubber installations use scrubber liquor and/or water (fresh or recycled) injected directly into the flue gas prior to the scrubber for the purpose of controlling relative humidity of the flue gas or its temperature. The excess liquid is then carried into the scrubber. Here also are two potential addition points for the introduction of the hypoiodite. 
         [0030]    The addition of the hypoiodite can be made in any of these locations, wholly or fractionally (i.e., a single feed point or multiple feed points), including but not limited to the make-up water for the lime or limestone slurry or the scrubber liquor. 
         [0031]    In some embodiments, bromide is available as iodine salt or iodic acid (HI) from an upstream process to the scrubber. The bromide salt may be in the form of calcium iodide (CaI 2 ), sodium iodide (NaI), or other iodide salts or as a mixture of various iodide salts. Hypoiodite is formed by adding an oxidant to the stream containing the iodine salt to generate hypoiodite in situ. The oxidant may be added to the scrubber liquor, low solids liquor return, virgin liquor, dispersion water, or other liquid existing during the capture, recovery, and treatment process. 
         [0032]    Often, the recovery of desirable ore products involves refining the ore from materials that contain mercury. For example, phosphate is often extracted from phosphorite which contains mercury as a trace element. During refinement of the desirable phosphorous mineral, mercury can be liberated such during fertilizer manufacture. In such cases, the mercury passes into a scrubber fluid, for example, a sodium-based alkali that is used to capture sulfur dioxide (SO 2 ). The mercury can be removed using the processes described herein. 
         [0033]    As another example, gold ore processing often involves roasting the gold ore to oxidize and remove sulfide. The gas generated by sulfur burning in the roaster is scrubbed to remove the sulfur dioxide and other components which can be contaminated with mercury. Mercury can be removed from these off-gases to make the gold processing more environmentally desirable. 
         [0034]    Thus, techniques described herein can be used to remove contaminating amounts of mercury from off-gases arising from various ore processing and ore refineries processing those ores. 
         [0035]    The invention is illustrated by the proceeding descriptions and the following examples which are not meant to limit the invention unless otherwise stated in the claims appended hereto. 
       EXAMPLES 
       [0036]    Testing for elemental mercury oxidation or absorption was performed using a multiple impinger setup with an inline mercury analyzer. The inline mercury analyzer for this testing was an Ohio Lumex RA-915 Portable Zeeman Mercury Analyzer. 
         [0037]    Referring to  FIG. 1 , a multiple impinger setup (with impingers serially connected: 1 to 2, 2 to 3, 3 to 4, etc.) was used to expose samples with elemental mercury. In Impinger  1 , elemental mercury was added (200 ppt, 5 mL) and combined with stannous chloride (2 mL) to evolve elemental mercury. In Impinger  2 , 30 mL of solution was added. The solution can be a diluted sample, synthetic slurries, test slurries, deionized (DI) water (for calibration and reference) or any combination of the above. In Impingers  3 - 4 , various solutions (30 mL) were added to reduce the amount of volatile material reaching the detector and not affect the mercury signal. These various solutions included HNO 3  and NaOH solutions at concentrations from 0.1 to 1 M. During calibration, these materials are replaced with the same volume of DI water. In the last impinger—Impinger  3 ,  4  or  5 , depending on the system—was left empty to catch any liquid overflow. The mercury detector was then connected to the last impinger followed by a carbon trap and pump. The pump draws ambient air from the room where the impingers are located. 
         [0038]    The second impinger used for this application was not a typical bottom draining impinger. Instead, a 100 mL round bottom flask was fitted at the bottom of the impinger so that the flask could be lowered into a heating bath for variable temperature measurements and was large enough for a variety of test solution volumes. The solution was bubbled with gas through a disposable pipette. 
         [0039]    Test slurries used were obtained from a commercial limestone forced oxidation wet flue gas desulfurization scrubber at a coal-fired electrical generator unit firing eastern bituminous coal. The pH of the slurry is typically between 5.5 and 6.5. 
       Example 1 
       [0040]    Adding potassium iodide (KI) in a 1:10 wt % of KI to hypochlorite in solution generated hypoiodite.  FIG. 2  shows a plot of the measured concentrations of sodium hypochlorite alone, sodium hypochlorite with potassium iodide and hypoiodate from the sodium hypochlorite/potassium iodide solutions associated with the percent of mercury removal from a synthetic slurry comprising 20 wt % CaSO 4 . The generation of hypoiodite increased elemental mercury removal from flue gas when compared to hypochlorite alone. 
         [0041]    Mercury removal in  FIG. 2  is calculated using the amount of elemental mercury not captured ([Hg 0 ] NC , mercury detected at the detector) compared to the amount of mercury initially in the system ([Hg 0 ] I  (Equation 1). 
         [0000]    
       
         
           
             
               
                 
                   
                     Hg 
                      
                     
                         
                     
                      
                     Removal 
                      
                     
                         
                     
                      
                     
                       ( 
                       % 
                       ) 
                     
                   
                   = 
                   
                     
                       ( 
                       
                         1 
                         - 
                         
                           
                             
                               [ 
                               
                                 Hg 
                                 0 
                               
                               ] 
                             
                             NC 
                           
                           
                             
                               [ 
                               
                                 Hg 
                                 0 
                               
                               ] 
                             
                             I 
                           
                         
                       
                       ) 
                     
                     × 
                     100 
                   
                 
               
               
                 
                   ( 
                   
                     Equation 
                      
                     
                         
                     
                      
                     1 
                   
                   ) 
                 
               
             
           
         
       
     
         [0042]    Comparative Example 1 
         [0043]    To test the saturation of elemental mercury in water, a known amount of elemental mercury vapor was bubbled through deionized water in a plastic jug using a Mercury Instruments MC-3000 Mercury Calibrator. A mercury generator was employed to create vapor phase elemental mercury (29 or 270 μg/m 3 ) with a N 2  carrier gas (2.5 L/min). This gaseous mixture was then bubbled through deionized water (0.9 L) for a varying amount of time (1-20 min). A small amount of water was then removed for analysis on an Ohio Lumex RA-915 Portable Zeeman Mercury Analyzer. 
         [0044]    The retention of elemental mercury in water over time was also tested using the same testing setup and procedure as above with one addition. After bubbling mercury through the deionized water for a set amount of time, the mercury ampule was bypassed so that only N 2  gas would flow through the deionized water. 
         [0045]    Elemental mercury was bubbled through deionized water to determine the saturation of elemental mercury in a system more similar to the dynamic system in a wet flue gas desulfurizer scrubber. The results shown in Table I indicate that the system was driving towards a steady state of ˜60 ppt and ˜700 ppt, at 29 μg/m 3  and 270 μg/m 3  respectively, rather than increasing up to the saturation limit of 60 ppb (60,000 ppt) all at 25° C. The initial concentrations at short times are higher than expected due to an oversaturation of the nitrogen carrier gas in the head space of the mercury ampoule, causing a burst of elemental mercury at the beginning of each test. Over time in both the low and high concentration systems, the concentration of elemental mercury drives to an equilibrium value. The theoretical values in Table I refer to the total amount of elemental mercury flow through the testing system based on concentration, flow rate and time. 
         [0000]    
       
         
               
               
               
             
               
               
               
             
               
             
               
               
               
             
               
             
               
               
               
             
           
               
                 TABLE I 
               
             
             
               
                   
               
               
                 Elapse Time 
                 Hg 0  in water, (ppt) 
                   
               
             
          
           
               
                 (min) 
                 Theoretical* 
                 Actual 
               
               
                   
               
             
          
           
               
                 Gas: 29 μg/m 3  and 2.5 L/min 
               
             
          
           
               
                 1.0 
                 146 
                 235 
               
               
                 2.5 
                 309 
                 137 
               
               
                 5.0 
                 521 
                 93 
               
               
                 10.0 
                 937 
                 61 
               
               
                 15.0 
                 1,342 
                 58 
               
             
          
           
               
                 Gas: 270 μg/m 3  and 2.5 L/min 
               
             
          
           
               
                 1 
                 349 
                 601 
               
               
                 10 
                 6,139 
                 701 
               
               
                 20 
                 21,139 
                 667 
               
               
                   
               
             
          
         
       
     
         [0046]    The saturation of elemental mercury in water was driving to equilibrium as governed by Henry&#39;s Law (Equation 2 below). Henry&#39;s law is defined as Henry&#39;s constant (K H , 376 atm at 25° C.), mole fraction of elemental mercury in solution (x), and partial pressure of elemental mercury (p, atm). Below in Table II are the theoretical values of elemental mercury in water based on Henry&#39;s Law and the concentration of the gas flowing through the system. The values are not exactly the same as the actual measured values but are on the same order of magnitude. These predictions are significantly lower than the solubility limit of 60 ppb for elemental mercury in pure water. 
         [0000]    
       
         
           
             
               
                 
                   
                     K 
                     H 
                   
                   = 
                   
                     p 
                     x 
                   
                 
               
               
                 
                   ( 
                   
                     Equation 
                      
                     
                         
                     
                      
                     2 
                   
                   ) 
                 
               
             
           
         
       
     
         [0000]    
       
         
               
             
               
               
               
             
               
               
               
             
               
               
               
             
           
               
                 TABLE II 
               
             
             
               
                   
               
               
                 Elemental Mercury Concentration 
               
             
          
           
               
                 Gas Phase 
                 Water Phase (ppt) 
                   
               
             
          
           
               
                 (μg/m 3 ) 
                 Actual 
                 Theoretical* 
               
               
                   
               
             
          
           
               
                 29 
                 60 
                 103 
               
               
                 270 
                 700 
                 963 
               
               
                 0.3 
                 — 
                 2 
               
               
                 5.0 
                 — 
                 18 
               
               
                 16,823 
                 — 
                 60,000 
               
               
                   
               
             
          
         
       
     
         [0047]    Next, these same solutions were tested for mercury retention or stability by first adding elemental mercury to the water in the same manner as above and then bypassing the elemental mercury ampoule so that only N 2  gas (elemental mercury content of zero) bubbles through the water for a varying amount of time. This would approximate the effect of a forced oxidation system in the wet flue gas desulfurizer scrubbers. In Table III, it can be seen that the elemental mercury was quickly removed from the deionized water by the pure N 2  gas. This behavior is also consistent with Henry&#39;s Law as the elemental mercury in the water phase transfers to the gas phase, the system continuously shifts in order to reach equilibrium. Elemental mercury was not readily soluble or retained in deionized water. 
         [0000]    
       
         
               
               
               
             
               
             
               
               
               
             
               
             
               
               
               
             
               
             
               
               
               
             
               
             
               
               
               
             
           
               
                 TABLE III 
               
               
                   
               
               
                 N 2  flow time (min) 
                 Hg (ppt) 
                 % retention 
               
               
                   
               
             
             
               
                   
               
             
          
           
               
                 29 μg/m 3  at 2.5 L/min for 1 min 
               
             
          
           
               
                 0 
                 297 
                   
               
               
                 1 
                 174 
                 59% 
               
               
                 2.5 
                 71 
                 24% 
               
               
                 5 
                 14 
                  5% 
               
             
          
           
               
                 29 μg/m 3  at 2.5 L/min for 10 min 
               
             
          
           
               
                 0 
                 76 
                   
               
               
                 1 
                 46 
                 61% 
               
               
                 2.5 
                 18 
                 24% 
               
               
                 5 
                 3.4 
                  4% 
               
             
          
           
               
                 270 μg/m 3  at 2.5 L/min for 1 min 
               
             
          
           
               
                 0 
                 601 
                   
               
               
                 1 
                 374 
                 62% 
               
               
                 2.5 
                 157 
                 26% 
               
               
                 5 
                 35.7 
                  6% 
               
             
          
           
               
                 270 μg/m 3  at 2.5 L/min for 10 min 
               
             
          
           
               
                 0 
                 701 
                   
               
               
                 1 
                 439 
                 63% 
               
               
                 5 
                 90 
                 13% 
               
               
                 10 
                 5.4 
                  1% 
               
               
                   
               
             
          
         
       
     
         [0048]    The data in these tables clearly define the problem by demonstrating that water-based scrubber liquors do not effectively decrease elemental mercury concentration in combustion flue gas. 
         [0049]    It is clear from these bench-scale results that the hypoiodite successfully and unexpectedly controls the emission of mercury from a scrubber by decreasing the elemental mercury flue gas concentration and does so more efficiently than conventional techniques. 
         [0050]    It should be understood that various changes and modifications to the presently preferred embodiments described herein will be apparent to those skilled in the art. Such changes and modifications can be made without departing from the spirit and scope of the invention and without diminishing its intended advantages. It is therefore intended that such changes and modifications be covered by the appended claims.