An Electrochemical Process for Simultaneous Treatment of Metal and Cyanide Bearing Wastewater

Heavy metal and cyanide contamination in electroplating wastewater can pose a serious environmental problem if not removed prior to discharge (Rajeswari and Sailaja 2014). Electrocoagulation has been shown to effectively remove many of these contaminants separately using batch treatment systems (Adhoum et al. 2004). The present study seeks to test the technologic efficacy of mixed electrocoagulation and hydroxide precipitation to simultaneously treat metals common to the electroplating industry (Ni, Cu, Sn), and cyanide (CN). The ultimate goal of the study is to offer a process which has the potential for use in continuous treatment. Cyanide ion (CN) begins to form volatile and dangerous hydrogen cyanide (HCN) in increasing concentrations as the pH drops below 11. At the same time, literature shows a drop-off in metal removal efficiencies using electrocoagulation at pH’s above 10 (Kobya et al. 2010). To overcome this drop, process variables such as current density, agitation rate, and volumetric flow rate of air were optimized using removal speed and final concentration as the chosen metrics. The data followed first and pseudo-first order kinetics which allowed the rate constants to gauge the relative rates of removal. The present work was able to reduce Ni, Cu, Sn and CN concentrations below the discharge limits set forth by the United States Environmental Protection Agency (EPA). The electrocoagulation cell conditions were optimized at a current density of 50 ASF, spin speed of 0 RPM, and volumetric flowrate of air of 0.0022 ft/min. This, along with a treatment time of 112 minutes, yielded an electricity consumption of 0.0206 kwh/L and an iron consumption of 3.83g/L. The study showed aeration to be necessary in achieving EPA discharge limits for complex cyanide removal. The use of aeration decreased the final concentration of complex cyanide from 4.1 to 0.91 mg/L after 2 hours of treatment. Testing also revealed direct reduction of metallic contaminants to the cathode to be another method of removal. Overall, the study shows electrocoagulation to be technologically and economically viable when treating high speed electroplating effluent. Due to the chosen conditions, the process also has the possibility of being extended to continuous treatment in the future.

The present study seeks to test the technologic efficacy of mixed electrocoagulation and hydroxide precipitation to simultaneously treat metals common to the electroplating industry (Ni +2 , Cu +2 , Sn +2 ), and cyanide (CN -). The ultimate goal of the study is to offer a process which has the potential for use in continuous treatment.
Cyanide ion (CN -) begins to form volatile and dangerous hydrogen cyanide (HCN) in increasing concentrations as the pH drops below 11. At the same time, literature shows a drop-off in metal removal efficiencies using electrocoagulation at pH's above 10 (Kobya et al. 2010). To overcome this drop, process variables such as current density, agitation rate, and volumetric flow rate of air were optimized using removal speed and final concentration as the chosen metrics. The data followed first and pseudo-first order kinetics which allowed the rate constants to gauge the relative rates of removal.
The present work was able to reduce Ni +2 , Cu +2 , Sn +2 and CNconcentrations below the discharge limits set forth by the United States Environmental Protection Agency (EPA). The electrocoagulation cell conditions were optimized at a current density of 50 ASF, spin speed of 0 RPM, and volumetric flowrate of air of 0.0022 ft 3 /min. This, along with a treatment time of 112 minutes, yielded an electricity consumption of 0.0206 kwh/L and an iron consumption of 3.83g/L.
The study showed aeration to be necessary in achieving EPA discharge limits for complex cyanide removal. The use of aeration decreased the final concentration of complex cyanide from 4.1 to 0.91 mg/L after 2 hours of treatment. Testing also revealed direct reduction of metallic contaminants to the cathode to be another method of removal. Overall, the study shows electrocoagulation to be technologically and economically viable when treating high speed electroplating effluent. Due to the chosen conditions, the process also has the possibility of being extended to continuous treatment in the future.
iv ACKNOWLEDGMENTS First I would like to thank my major professor Dr. Otto Gregory. Not only were the 2 classes I took with you, both undergraduate and graduate, some of my favorites in the Chemical Engineering curriculum, but you showed support and lent advice to a student who wanted to take the next step in his education but wasn't quite sure which way to go.
Next I would like to thank the management team at Materion Technical Materials in Lincoln RI. Trying to further your education while working full time is a difficult endeavor. The support and understanding they showed during the past 3 years has been critical to both my academic and industrial success. Hopefully the skills I have learned will be beneficial to the strength of the company, and we will all continue to grow.
Finally, I would also like to thank family and friends for their continuing support, especially Kim Maleski. Without her leading through example and showing constant encouragement I would not have been able to make it to this point.
v     xv GLOSSARY OF TERMS A Aggregation -In colloidal chemistry aggregation is the collection of units or parts into a mass or whole after destabilization has occurred. Amphoteric -A species which which can react by either donating or accepting a proton. ASF -English unit for current density equal to amps/ft 2 B Bipolar Connection -An electrode configuration in which sufficiently high electric field induces both cathodic and anodic reactions at the same electrode. Only 1 electrode is electrically connected to the power source. Boltzmann Constant -Equal to the ideal gas constant (R) divided by avogadro's constant (NA), it relates thermal energy at the microscopic level. Polymer Bridging -In wastewater treatment polymeric substances are often used to flocculate suspended particles from solution. The main mechanism for this action is active sites on the polymer which can be tuned to target specific contaminants. Once absorbed to the polymer it can settle out of solution due to the large molecular weight. Bulk Concentration -In electrochemistry the bulk concentration is the analyte concentration far enough from a charged surface where virtually no concentration gradient exists. C Characteric Concentration -In atomic absorption spectrometry the characteristic concentration is the analyte concentration which produces a 1% absorbance signal. This corresponds to 0.0044 absorbance units. Characteristic Concentration Check -In atomic absorption spectrometry the characteristic concentration check is the analyte concentration which produces a signal of 0.2 absorbance units. It represents a concentration which is high enough to reduce natural variation and is used to determine that the device is reading correctly. Charge Neutralization -Usually accomplised by relatively small salt additions, charge neutralization is accomlished when ions adsorb to the surface of a colloidal particle reducing the charge and allowing aggregation. Coagulation -In colloidal chemistry coagulation is the reduction of the repulsive forces keeping microscopic colloidal particles apart inducing flocculation. It can be accomplised by double layer compression, polymer bridging, charge neutralization or sweep flocculation. Colloid -A solution in which one microscopic substance is dispersed within another. It occurs in particles with a high surface area to mass ratio where intermolecular forces dominate the force of gravity. Colloidal Destabilization -See Coagulation Condensation Reaction -A polymerization reaction in which two molecules combine to form a larger molecule releasing smaller one. Most commonly this smaller entity is water. Current Density -A common metric in electrochemistry, current density is the current being passed through an electrode divided by the surface area of the electrode. It is used to estimate and compare mass transport limitations. D DLVO Theory -A theory describing the forces present within colloids. It is named using the initials of its founders Boris Derjaguin, Lev Landau, Evert Verwey, and Theodoor Overbeek. Attractive forces are commonly modeled using van der Waals interactions. Repulsive forces are commonly modeled using electrostatic repulsion. At the center of the theory it uses the net attraction or repulsion derived by summing these 2 forces to predict the state of the colloid. Debye length -A measure of the distance from an electric charge in solution in which electrostatic effects still persist. At distances larger than this length the charge is effectively screened. Double Layer Compression -When a large amount of salt is added to a colloidal dispersion the charges begin to oppose the electrical double layer which in turn compresses its effects. Once a threshold is reached the colloid destabilizes and begins to aggregate. E Electrical Double Layer -In solution electrochemistry an electrical double layer is the approximately two atom thick layer of oppositely charged particles which forms on a charged surface in solution. Electrocoagulation -The use of a dissolving iron or aluminum anode to electrochemically treat wastewater through sweeping hydroxide flocculation. Electrostatic Repulsion -The repulsive force which arises when 2 like charges approach each other in solution. It is an exponential function of distance for 2 small spheres. F Ferric Ion -Iron containing materials in which the iron oxidation state is +3. Ferrous Ion -Iron containing materials in which the rion oxidation state is +2. Flocculation -Reversible association in which individual particles aggregate after destabilization. Floccule -A group of reversibly aggregated particles. G Ground State Atom -The electron configuration of an atom at its lowest energy state H Half Life -In reaction chemistry it is the amount of time required for an analyte to reach half of its initial value. Hamaker Constant -In colloidal chemistry the hamaker constant is a numerical value, derived from experimentation, that represents the attractive van der Waals forces between 2 objects through a specific medium. Hydroxide Precipitation -The use of pH to drive dissolved metal equilibrium toward hydroxide formation. It is often used in waste water treatment. I Inverse Debye Length -1 divided by the debye length. L Linear Range -In Atomic absorption spectrometry, the linear range represents the maximum analyte concentration for a particular wavelength in which the absorption in still linear with respect to concentration.
xvii M Monopolar Connection -An electrical connection in which the positive and negative electrodes are separated by the working solution and connected. Both electrodes are connected to the electrical source. R Relative Noise -In atomic absorption spectrometry the relative noise is a neumerical value used to represents the instability inherent in each wavelength. It is used to decide the best wavelength for the sample being tested. S Sedimentation -A physical process in which gravity causes suspended particles to settle out of solution. Slit Size -In atomic absorption spectrometry the slit size is the physical measurement of the orifice through which the wavelength passes for measurement. Often on the order of nanometers, larger slit sizes usually offer higher sensitivity. Stern Layer -See electrical double layer U Ultrafiltration -A type of filtration which employs size exclusion through the use of membranes and a pressure gradient to separate materials. V Van der Waal Forces -Attractive forces which arise at short distances. Can be the result of induced dipoles, permanent dipoles or hydrogen bonding.

INTRODUCTION
Wastewater treatment represents a substantial cost associated with electroplating facilities. As such there will always be an economic driver to reduce its cost. Even though there is a financial incentive to treating wastes and reducing contaminants in wastewater streams, the more important issue is the protection of the environment. Treating effluent is the final step in any industrial electroplating process. Therefore, it becomes paramount to remove any heavy metals and cyanide from waste streams, which would otherwise damage the environment. As such, it must not only be an economically viable process, but must be technologically able to meet the stringent regulations set forth by the United States EPA.

INDUSTRY STANDARD
Hydroxide precipitation is the main method of heavy metal water purification As shown in figure 1, there is no single pH value which will remove all the metals above to EPA permissible levels. Depending on the target metals, this may lead to multiple pH adjustments followed by sedimentation and filtration to remove the insoluble hydroxides separately. The duplication of equipment necessary to insure precipitation and removal only serves to increase the capital cost with these systems.
The pH adjustments are typically done using Ca(OH)2 (lime) or NaOH (caustic).
Calcium hydroxide is usually preferred due to its lower cost but comes with the caveat of increasing sludge generation. This sludge must be removed through sedimentation and ultrafiltration or bridging polymers prior to discharge.
Wastewater from most precious metal electroplating plants will typically contain cyanide (Amarnath et al. 2014). This is because cyanide forms complexes with gold and silver and are widely used in precious metal electroplating baths (Schesinger and Paunovic 2010). Cyanide is a poisonous chemical which readily forms strong complexes with many non-precious metals as well. This causes treatment to be more difficult. It also forms dangerous and volatile hydrogen cyanide gas according to the conditions shown in figure 2 below. As shown, the concentration of hydrogen cyanide created is a function of pH.
Above a pH of 11, the cyanide remains completely dissolved in the form of CN -.
Below a pH of 7, all of the cyanide present is converted to molecular HCN. HCN has a boiling point of 299K at atmospheric pressure, and a vapor pressure of 0.80 ATM at room temperature (20 C) (National Institute of Standards and Technology). This information gives some insight into the high evaporation rate of hydrogen cyanide under ambient processing conditions.
The standard chemical process for the treatment of cyanide involves two steps.
The first step is oxidation of cyanide ion to cyanate ion at a pH of at least 10 using sodium hypochlorite (chlorine bleach). The second step is the conversion of the cyanate ion to volatile and non-poisonous carbon dioxide and nitrogen gas using additional sodium hypochlorite. This reaction occurs fastest at a pH of 8.5 (Amarnath et al. 2014).

ELECTROCOAGULATION BASICS
Electrocoagulation, or the use of electricity and iron plates to treat wastewater, is not a new idea. The concept dates back to the late 1800's with the first patent for "purification of wastewater by electrolysis using corroding electrodes" submitted in 1909 (Vik 1984). In electrocoagulation, a sacrificial anode is used to supply metal ions to an aqueous solution. Aluminum and iron are the most widely used anode/cathode plate materials. Since iron has shown greater removal efficiency and is less expensive, we will focus on reactions involving it as the electrode material in the proposed study (Moussavi et al. 2011).
The reactions based on an iron plate electrode proceed as follows: Figure 4: Formation of iron and hydroxide ions during electrocoagulation (Kobya et al. 2010) Iron ions generated at the anode combine with hydroxide ions, either generated at the cathode or present in solution by starting pH, to form insoluble iron hydroxides.
These hydroxides can undergo polymerization/condensation reactions as follows: Figure 5: Iron hydroxide polymerization/condensation reaction (Kobya et al. 2010) The polymerized iron hydroxides form large three-dimensional structures, which are largely insoluble and precipitate from solution. Metal ions and colloidal particles adsorb onto these surfaces as the coagulation process proceeds. This mechanism is responsible for destabilization and final aggregation of the material targeted for removal (Kobya et al. 2010).
Figure 6: Proposed mechanism for pollutant removal during electrocoagulation (Kobya et al. 2010) In addition to the chemical aspects of metal removal, the conditions in the electrocoagulation cell can also be optimized to concentrate the metals based on hydrodynamics. This is illustrated in the following figure.
Figure 7: Physical processes occurring within electrocoagulation (Holt et al. 2002) As shown in Figure 7, the hydrolysis of water creates two regions of concentrated floc.
Hydrogen gas formed at the cathode rises to the surface in the reactor. This motion tends to move or sweep the newly formed floccules towards the surface as they become entrained by the gas bubbles. If the floccule does not become entrained, it will eventually settle to the bottom of the tank in a more typical fashion. The relative amounts of surface vs. bottom sludge can be controlled by gas generation. This is typically a function of current density at the cathode and solution agitation (Holt et al. 2002). Having areas of concentrated waste can be beneficial by streamlining subsequent filtration steps.
In addition to increased agitation through gas bubble generation, higher current densities also increase the rate of contaminant removal through anode dissolution. It stands to reason that as you increase the current in the system your anode will dissolve quicker. This leads to higher concentrations of iron hydroxide floc at shorter treatment times which in turn can reduce total treatment time (Dermentzis et al. 2011).

BASICS OF COAGULATION AND FLOCCULATION
Electrocoagulation has been shown to effectively treat both dissolved and colloidal material (Matteson et al. 1995, Kobya et al. 2010. A colloid is a homogeneous mixture where one insoluble phase is dispersed in another. Extremely small particles (0.001 to 10µm) tend to have a large surface area to mass ratio. Under these conditions intermolecular forces dominate the force of gravity and thus the dispersed phase remains dispersed (Ghernaout and Ghernaout 2012). Coagulation is the irreversible reduction of the forces which serve to keep these particles apart.
Flocculation is the reversible agglomeration of the particles into larger particles once coagulation has occurred.
DLVO theory can be used to help explain the forces in a typical colloidal system. In this theory, the 2 main forces at work are electrostatic repulsion and Van der Waals attraction. Electrostatic repulsion is a function of the surface charge of the colloid. It increases exponentially as the 2 surfaces approach each other. The following is the equation for electrostatic repulsion of 2 charged spherical objects at very small separations (kh>>1, R1 and R2 >> h) (Evans and Hakan 1999): = 128 1 2 1 + 2 * г 10 г 20 (− ℎ) Both the electrostatic repulsion force and Van der Waals Forces can be added and plotted as a function of inter-particle distance. If an energy barrier exists, the 2 surfaces will not be able to get close enough to flocculate and a colloid is formed.  Polymer bridging uses long chain polymers to intertwine colloidal particles ( Figure   12). Longer chain polymers work better than small chain and active groups can be adjusted to target specific contaminants for removal.

CHEMICAL REACTION KINETICS
Classical reaction kinetic theory shows it is possible to assign constants indicative of the reaction rate. Reactions are classified by the order in which they depend on reactant concentration and will be explained in detail in the following paragraphs. It is possible to use timed conversion data to solve for these constants graphically. Ultimately these constants can be used to compare reaction rates which becomes a good gauge of reaction speed.
The differential form of a zero order reaction can be written and integrated as follows: In a zero order reaction the reactant concentration decreases linearly with time.
A plot of the concentration of these reactants vs. time will yield a straight line. The In a first order reaction, the decrease in concentration of reactants with respect to time is proportional to the concentration. This means that as the reactant concentration decreases, so too does the apparent contaminant removal rate. The differential form of a first order reaction can be written and integrated as follows: 13 As you can see, in a first order reaction a plot of the natural log of concentration vs.
time yields a straight line. The slope of this straight line is the kinetic constant and the y-intercept is the natural log of the initial concentration.
Half Life In a second order reaction the reaction rate is proportional to the reactant concentration to the second power. These reactions tend to move faster due to the inverse relationship which appears after integration. The differential form of a second order reaction can be written and integrated as follows: As you can see, a plot of the inverse concentration vs. time yields a straight line. The slope of this line is the kinetic constant and the y-intercept is equal to the inverse initial concentration.
Half Life Upon starting the experiments in this report, it was quickly apparent that the conductivity of DI water (<20 µS/cm) was insufficient to carry the current necessary to reach the 75 ASF target. Sodium chloride was chosen to increase the conductivity due to low cost and availability. A theoretical analysis on ideal salt concentration was then performed. It took into account 3 factors of operation; salt cost, electricity consumption, and iron consumption.
Electricity consumption is measured in watt hours or more typically kilowatt hours. A kilowatt hour is equal to; The average electricity cost for the United States in 2015 was $0.1096 per kilowatt hour (eia.gov/electricity/monthly electricity).
In electrocoagulation the amperage and time are fixed by ideal cell operation.
Changing one of these factors can negatively affect the contaminant removal efficiency which will become apparent in the following sections. The only variable of the 3 listed which can be modified to reduce cost is voltage. Conductivity of salt water solution increases linearly with salt concentration (Lide 1994).     The first test conducted showed the effects of current density on waste removal. The chosen current densities were 2.5, 5, 7.5, and 10 mA/cm 2 . The results showed that the ideal anode-cathode configuration is dependent on the type of metal targeted for removal. Copper removal occurred fastest using an iron anode and cathode. Nickel and chromium removal occurred fastest under the iron-anode aluminum-cathode configuration. The iron-iron configuration was also comparable in reducing contaminants to permissible levels. All tests showed 10 mA/cm 2 to be the best current density for contaminant removal.
Next an initial pH of 3, 5, 7, and 9 were tested under the different configurations. Again the iron anode and cathode achieved the greatest copper removal efficiency, while the iron-anode aluminum-cathode worked best for chromium and nickel. And again, the iron-iron combination was not far off in terms of removal efficiency and speed of removal. Tests showed optimal removal conditions occurred at a pH of 9.
Finally, the effects of solution conductivity were tested. Sodium chloride was used to achieve conductivities of 2, 4, and 6 mS/cm. As you can see below, increasing conductivity increased the removal efficiency under most conditions.   After the removal efficiencies had been established, the study proceeded to investigate the reaction kinetics. This was done by fitting curves to the time dependent data and using a least-square method to determine the best fit. Three of the more common fits were explored in the introduction section of this paper. They found the best fit for the data was the pseudo-first order model which predicts the contaminant concentration approaches an equilibrium value (Ce) rather than zero.   Finally, the electrode and energy consumption were calculated. This was done using faradays law of electrolysis and the Amperage/voltage/time requirements normalized to treatment volume (see introduction). They found that full treatment required an energy and electrode consumption of 6.25-8.33 kWh/m 3 and 1.31-1.74 kg/m 3 respectively.

TREATMENT OF FREE CYANIDE
The next category is treatment of cyanide alone. Moussavi et al. 2011 were able to show a maximum of 98% cyanide removal using an iron-aluminum electrode arrangement as the anode and cathode respectively. Agitation was also tested utilizing aeration of the electrocoagulation cell. All experiments were carried out at an initial pH of 11.5, a current density between 2 and 15 mA/cm 2 (1.86 -13.94 ASF), and a reaction time between 20 and 50 min. The initial pH was presumably selected to ensure non-volatile ionic cyanide was present in the reactor.  Although the best results were achieved using the iron-aluminum couple, as you can see from the figure above, the iron-iron electrode achieved similar results.
Both of these arrangements performed markedly better than the aluminum-aluminum and aluminum-iron pairings (Moussavi et al. 2011).
An important result arises when examining the effects of increased current density in the following figure. In an attempt to explain the increase in removal efficiency the team ran another set of experiments quantifying the amount of sludge generated. To do this, trials were run with and without aeration for 20 minutes. They found that under aerated conditions the system produced approximately twice as much sludge. They theorized that the increase in sludge generation resulted from the oxidation of ferrous to ferric ion in the increased oxygen environment. This in turn led to a more gelatinous hydroxide precipitate and an increase in efficiency. It was pointed out that "The higher the precipitate (adsorbent) formation and effective contact of precipitates with the contaminant, the greater the adsorption rate and thus removal" (Moussavi et al. 2011). Aeration of the cell seems to serve both of these mechanisms in a positive way.
Hassani et al. 2011 also investigated the removal of cyanide through electrocoagulation using iron electrodes. Sodium bisulfite at a concentration of 300 mg/L was utilized to keep the oxidation state of iron to +2 and stabilize the cyanide in solution (Hassani et al. 2011). This then allowed them to run the reactor at a pH between 4.5 and 6 without fear of converting the free cyanide to hydrogen cyanide gas. After electrocoagulation was complete, the pH was again adjusted using sodium hydroxide between 8 and 8.5 to facilitate hydroxide precipitation and free cyanide removal by sweep flocculation.
The reactor consisted of 8 monopolar plates spaced 10mm apart. The main variables examined were operating voltage and starting concentration. As you can see in the following figure, the removal percentage maxed out at 97% after 90 minutes.
This was only achieved at cell voltages greater than 30 which adds to operating cost.  As you can see from the figures above, the initial pH for optimal cyanide removal from the nickel cyanide solution was between 8 and 10 with a sharp decrease in removal efficiency outside this range. The initial pH for optimal cyanide removal from the cadmium cyanide solution was between 6.5 and 10.5 with a much slower rate of drop outside this range. This difference may be an artifact of the different starting metal-cyanide concentrations. It may also indicate that the type of metal complex affects the ideal electrocoagulation operating conditions. It is also important to note that both graphs show a decrease in removal efficiency at pH's greater than 10 -10.5.

Senturk (2013) investigated electrocoagulation for the treatment of zinc-
cyanide exploring a few more operating variables than Kobya et al. (2010). The focus of this paper was current density, 2.5-40 A/M 2 , operating time (0-60min), initial pH (5-12) and electrode connection mode (monopolar parallel, monopolar series, and bipolar series). They utilized electrodes with a total area of 225 cm 2 , spaced 10mm apart in a 1 L electrocoagulation unit yielding a surface area to volume ratio of 225 cm 2 /L. In these experiments the maximum removal efficiency occurred at an initial pH of 9.5 using iron electrodes. These conditions were then used in the next experiment testing the effects of current density.
C .   Since cyanide in solution forms volatile hydrogen cyanide gas below a pH of 11, this forms a necessary lower limit for this study. During operation it would pose a serious threat to safety if any cyanide being treated suddenly became volatile. As was pointed out in the introduction section, different metal-cyanide complexes may affect cyanide removal rates. A major point of the study is to determine how particular mixtures of metal complexes (Ni +2 , Cu +2 , Sn +2 ) affect cyanide removal. and CNconcentrations between 50 and 160 mg/L. The 160 mg/L tin concentration was purposely chosen higher than the rest due to the sensitivity of the atomic absorption unit and is further explained in appendix A. DI water with a conductivity less than 20 µS/cm was used to make up the remainder of the operating volume.

REAGENTS AND APPARATUS
Sodium chloride at a concentration of 5 g/L was added to increase electrical conductivity. All experimentation was carried out in a 3000 mL beaker filled to a 2500 mL operating volume using synthetic wastewater. This particular setup was chosen to accommodate the size of samples which must be pulled from the reactor for testing.
Temperature was measured at 25 C + 6 C using a Fisher Scientific Isotemp hotplate equipped with a temperature probe. The pH was measured using a portable pH meter (model pH 5+ made by Oakton Instruments) suspended by ring stand.

Figure 66: pH and Temperature Probe Suspended by Ring Stand
Initial pH adjustments were made using reagent grade hydrochloric acid and sodium hydroxide. Electrical power was supplied using a DC Rectifier (10V, 11A), made by Human Company in current regulation mode. G1000 series steel was used as the anode and cathode material due to low cost, high availability, and high iron content. The plate cross sectional area was approximately 2.25" x 6" wide and the plates were held 0.25" apart. Prior to each run the newly cut plates were activated in a 50% concentrated hydrochloric acid solution for 10 minutes.

SAMPLING PROCEDURE
60 mL samples were taken at selected intervals and the generated sludge was allowed to settle for 20 minutes by sedimentation prior to analysis.  Cyanide sampling has extra requirements. A 125 mL sample was taken at regular intervals out to 2 hours and 40 minutes run time. This is because prior literature has shown cyanide removal to occur much slower than metal removal (Moussavi et al. 2011). The concentration of cyanide will be analyzed using an outside laboratory in accordance with EPA standard SM4500CN-C E 18-21 ed.
This testing method uses distillation and an ion selective electrode or silver nitrate titration to measure the total cyanide concentration in solution (Greenberg et al. 1992). According to this standard, the samples must be preserved with sodium hydroxide to a pH of at least 11 and refrigerated prior to analysis. Since the initial pH was already set to 11 and only increases after operation begins, no further sodium hydroxide was needed for preservation. For plants discharging greater than 10,000 gal/day the limits are as follows:

CHOICE OF TEST VARIABLES
From previous literature, one of the more important characteristics of electrocoagulation operation seems to be current density (Senturk 2013). The current densities already published in the reviewed literature range from 0.5 to 45 ASF with higher current densities corresponding to decreased operating time, increased efficiency, and reduced costs (Kobya et al. 2010). To extend the data for current density the experiments were run at 25, 50 and 75 ASF.
The stir speed was varied from 0 to 300 RPM to investigate its effect on metal removal after sedimentation. As stated in the review of literature section, agitation is an important variable in electrocoagulation (Ghernaout and Ghernaout 2012). The prior literature shows incomplete removal of nickel and cyanide in a nickel(II) cyanide solution at an initial pH of 11 (Kobya et al. 2010). This increase in stir speed will serve to increase collisions of the flocculent with the targeted contaminants and may help overcome this incomplete removal shown by Kobya et al. 2010.
In addition to agitation by stir bar, the present study added aeration as an alternative. Aeration was shown by Moussavi et al. 2011 to increase both the speed and percentage of free cyanide removal at a pH of 11.5. The author postulated that oxidation of ferrous to the more gelatinous ferric hydroxide in the increased oxygen environment was to blame for this increase in removal efficiency. It is hypothesized that this effect may help to overcome the incomplete nickel cyanide removal shown by Kobya et al. 2010. A Fisher scientific desktop vacuum filtration pump was used to introduce air to the reactor. The air speed was adjusted via regulator seeking a flow rate low enough to prevent shear induced breakage of floccules, but high enough to induce conversion of ferrous to ferric hydroxide.
Attempts were also made to model the data using traditional reaction kinetic theory (0, 1 st , pseudo-1 st , or 2 nd order). As outlined in the introduction section, one can find the kinetic constants associated with a first order chemical reaction through a plot of the natural log of concentration vs. time which should be a straight line. The negative of the slope is the reaction rate coefficient. These were used to gauge the difference in removal speed for each trial.

HYPOTHESES
The present work set out to develop a process which could be used to treat both heavy metals and cyanide simultaneously and continuously using electrocoagulation and hydroxide precipitation. This goal led to the formation of a few different hypotheses. First, since tin is a vitally important element to the electronics industry, it was hypothesized that at a pH of 11 electrocoagulation or hydroxide precipitation would be able to reduce tin concentrations below EPA permissible levels. Moussavi et al. 2011 showed that aeration could be used to increase the removal percentage of free cyanide to 100%. Kobya et al. (2010) and Akbal and Camci 2011 both showed a decrease in nickel-cyanide removal at pH's greater than 10. They both postulated that at higher pH's the iron in solution only forms monomeric iron hydroxide verses the large polymeric hydroxides ideal for sweep flocculation. Since Moussavi et al. 2011 linked the increase in cyanide removal efficiency observed from aeration to the change of ferrous to ferric ion, this transition may be beneficial to nickel-cyanide removal as well. It is therefore hypothesized that aeration could be used to help overcome the apparent decrease in nickel-cyanide removal efficiency observed at high pH, and reduce metal-cyanide complexes to EPA permissable levels.
The final goal of the project was to apply reaction kinetic theory to the data obtained during testing. The hypothesis being that zero, first, or second order reaction kinetics would accurately reflect the data observed.

TIN SOLUBILITY DATA
The first step of this research was to determine whether hydroxide precipitation or electrocoagulation would be the main method of removal at a pH of 11 without the presence of cyanide. This was accomplished by creating a solution with approximately 160 mg/L of Sn +2 in DI water and pulling samples as the pH is adjusted. The tin hydroxides in these samples were allowed to settle by sedimentation prior to testing. Below is the graph of the data. However, the monthly average discharge limit in Rhode Island is 2.00 mg/L meaning an alternative form of treatment would be required before discharging.

EFFECT OF CYANIDE CONCENTRATION ON METAL SOLUBILITY
In a typical electroplating job shop the amount of discharge and concentration of contaminants is constantly changing. This is because all lines do not run 100% of the time, and the different geometries being processed tend to change contaminant levels incoming to wastewater treatment. In initial experiments it became clear that the addition of cyanide increased the concentration of all metallic contaminants. As stated earlier, cyanide readily forms complexes with various metals in solution (Griffith 1962). It seems that the addition of cyanide favored the formation of these complexes over hydroxides at the pH being tested. The amount of metal which "redissolved" was a function of cyanide concentration and increased until the starting concentrations of the waste stream were reached.
This ability to re-dissolve originates from the set of equilibrium reactions taking place in the electrocoagulation cell. As you can see below, the equilibrium constants greatly favor the formation of the cyanide complexes, further supporting the data.
Hydroxide Formation (Hill et al. 2005) Cu +2 + 2OH -↔ Cu(OH)2(s) Ksp = 2.2e-20 In all experiments the contaminant metal levels were reduced below EPA permissible discharge limits by minute 60. This proved the first hypothesis correct.
Electrocoagulation can be used to treat Tin +2 at a pH of 11. The rate at which these metals were removed changed with current density as evident by the first order rate constants. Both tin and coper removal peaked at 50 ASF. Nickel removal didn't vary as much as the tin and copper with respect to current density. From this information the optimal current density chosen for spin speed and cyanide experiments was 50 ASF.
One would expect that as the current density increases so too would the contaminant removal. This is because the iron dissolution rate increases with current density and ultimately the iron hydroxide floc concentration rises faster. This was not observed during experimentation. Some explanation has already been given for this effect by Adhoum et al. 2004 andSenturk 2013. They postulated that as the bubble generation rate increases the iron hydroxide floc is swept straight to the top of the    This causes more copper hydroxide to dissolve to Cu +2 + 2OHwhich ultimately reacts with free cyanide to form [Cu(CN)4] -3 . Thus at low treatment times the copper concentration may remain fairly constant due to a slow equilibrium step, or until all the copper has completely reacted.
Another possible explanation is the competition between different metals for removal through the various mechanisms present. This could either be direct electrochemical reduction to the cathode surface or adsorption/enmeshment into the growing floc.
To test these theories another 3 sets of tests were run at 50 ASF, and 0 RPM.
The first 2 varied the initial concentration of copper (24 and 72 mg/L). If the equilibrium is to blame for the departure from first order kinetics then adding more copper should yield even longer departure times before first order kinetics set in. In contrast, the lower copper concentration should yeield shorter departure times.
The third test removed tin and nickel from solution focusing only on copper metal. To ensure insoluble copper hydroxide remained present, and thus the possibility of equilibrium effects, the cyanide concentration was lowered to 10 mg/L.
If competition is truly to blame then even with copper hydroxide present there should be an immediate decrease in concentration during operation.

Time (Minute)
However, as observed in the literature, cyanide removal occurred much slower than metal removal and thus becomes the largest contributer to operating cost.

CYANIDE REMOVAL: WITH AERATION
As stated in the experimental procedure section, Moussavi et al. was able to show an increase in the rate of free cyanide removal through the use of aeration.
Though free cyanide and complex cyanide removal have been shown to exhibit different removal characteristics (Moussavi et al. 2011, Kobya et al. 2010, the use of aeration was also tested in this experiment. The hypothesis again being increased conversion of ferrous to ferric iron hydroxide would create a more gelatinous floc and should increase the rate of complex cyanide removal. Three different air flow rates were tested (0.00209, 0.004189, 0.006283 ft 3 /min).

INSOLUBLE ANODE
When running these experiments it quickly became apparent that electrocoagulation and hydroxide precipitation were not the only methods of metal removal occuring. As you can see in the picture below, the cathode at the end of each experiment showed a copper colored hue. This copper layer indicates direct reduction of copper metal from solution to the cathode during operation (electroplating). Electroplating is strongly dependent on solution agitation at high current density. This may explain the increase in removal rate experienced by copper at higher spin speeds. It may be that with no agitation, electrocoagulation is the main method of removal. At low spin speeds of 50 and 100 RPM there is enough agitation to induce breakage and reduce flocculation efficiency.
At higher agitation levels the main mechanism may shift to electroplating due to availability of metal ions at the cathode surface.
To better understand the role of electroplating in these experiments another test was devised using an insoluble anode. With an insoluble anode, electrocoagulation is not a removal mechanism. This is because the anode no longer supplies iron ions to the working solution. A platinized titanium anode was chosen for this trial due to availability. Tests were run at 50 ASF and 300 RPM for comparison.

CONCLUSION
The goal of this thesis was to determine whether or not electrocoagulation could be used to treat metals in effluent streams common to the high speed electroplating industry, with a secondary goal if continuous treatment was plausible.
As described in this thesis, tin is an important metal in high speed electroplating. An in-depth literature search, indicated that electrocoagulation had not been considered for tin removal to date. Thus, the first part of this study showed that electrocoagulation could be used for the treatment of wastewater laden with tin and could be used to reduce concentrations down to EPA permissible levels.
This study also set out to test the ability to treat all of the metals common to the high speed electroplating industry and cyanide simultaneously in a single vessel at a pH of 11. This information was necessary if the system was to be used continuously in the future. The study showed that simultaneous treatment was possible at a starting cyanide concentration of 50 mg/L. Using a relatively simple setup, tin, nickel, and copper could be reduced to EPA dischargeable levels in under an hour.
Cyanide treatment proved to take the longest with a treatment time of 112 minutes. This treatment time is excessive and thus, becomes a limiting factor in treatment due to operating costs. Additional aeration treatments were determined to be the only way to achieve EPA discharge levels in a cost effective manner. This is due to conversion of ferric to ferrous iron, which creates a more gelatinous floc that is better suited to cyanide coagulation.
Finally, the electricity and iron costs were estimated for the electrocoagulation process. The current electrocoagulation process ran for 112 minutes, at 4.6 amps, 6 volts and treated 2.5 liters. This yields an electrical consumption of 0.0206 kwh/L and an iron consumption of 3.83g/L.

FUTURE WORK
The present work shows feasibility of an electrocoagulation process to treat both metals and cyanide in solution. It also raises a few questions, which must be answered by additional research before the technology can transferred to the end users; the wastewater treatment industry. The following issues need to be addressed before future research can focus solely on making the process more robust and cost effective.
The first and most obvious issue is an extension of the present research: that is to investigate continuous processing or continuous treatment of the waste streams generated by the electroplating industry. All testing to date was carried out in a batch process and thus, it is critical to determine how the batch process would translate into continuous one. Figure 76 shows the effect of cyanide concentration on metal concentration.
The present research showed that treatment using the electrocoagulation route is possible up to a starting concentration of 50 mg/L cyanide. The pseudo-first order rate law for this process indicates that the lowest final concentration possible for this initial concentration is 0.72 mg/L. To better understand the limitations of the process, further research should focus on the maximum initial cyanide concentration permissible to deliver a final concentration below the EPA limit of 1.0 mg/L.
Experiments run with an insoluble anode showed that electroplating was at least a part of the removal mechanism. This opens the possibility that future experimentation could reduce the operating cost of the system. If a system employing two sets of electrodes is used, the iron consumption and treatment time may be reduced if only one of them is an insoluble anode such as platinized titanium.
Optimization of factors such as individual current densities and/or cycle times may be important.

APPENDIX A: ATOMIC ABSORPTION PROCEDURE
All elemental concentrations in this thesis were obtained by atomic absorption spectrometry (AAS). In atomic absorption a ground state atom of the target element absorbs a specific wavelength of light. The more atoms in the beam path, the more light which is absorbed. By making fine measurements of this absorbance it can be used to determine the relative amount of certain elements suspended in solution.
The work contained used the PerkinElmer Pinnacle 900f, one of the newer models made by PerkinElmer. The following were the standard conditions chosen during experimentation: The relative noise is a factor used to quantify the variability of the signal. A lower value corresponds to a more stable reading. The characteristic concentration is the analyte concentration required to achieve a 1% absorbance signal at the specified wavelength. This corresponds to a signal of 0.0044 absorption units. The characteristic concentration check is the analyte concentration required to achieve a signal of 0.2 absorption units. It represents a concentration high enough to reduce natural variation and ensure the machine is operating correctly. Finally, the linear range represents the maximum concentration where the absorbance signal is linear with respect to concentration. Up to this concentration only a single standard needs to be used. Above this concentration the absorbance signal begins to curve. More standards must then be used to account for this curvature.
The wavelengths in the table above were chosen due to linear range, low characteristic concentration, and the 6:3:1 rule for each element. This rule states that the concentration of your lowest standard be at the top of the linear range with your next 2 standards 3 and 6 times this initial concentration (Analytical Methods for Atomic Absorption Spectrometry). The following standard concentrations were chosen to encompass the range of values expected in the testing. All blanks and standards were made to mimic the working solution. This included the addition of 5 g/L sodium chloride. The addition of sodium chloride served 2 purposes; reduction of matrix and possibly ionization interferences. A matrix interference occurs when the flow characteristics of the working solution vary from the standards. This includes factors such as density, viscosity, and surface tension.
By making the standard and blank with sodium chloride the densities will remain close. Ionization interference occurs when the energy of the flame is high enough to ionize the target metal rather than induce an excited state. This can be reduced by the addition of compounds which ionize easily. Alkali metals are typically used, and thus the sodium serves this purpose.
The detection limits of nickel and copper are lower than tin at the wavelengths chosen. This is a product of both the weaker signal from tin and the fact that Materion Technical Materials employs a pure acetylene flame. Greater accuracy may be attainable with a nitrous oxide enriched flame, but this was unavailable during testing.
To better quantify the statistical accuracy of tin at low and high concentrations, 10 readings of each were taken with blanks in between. The blank reading before and after was averaged and subtracted from the concentration reading. The following formula was used to determine the detection limit: Assuming a normal distribution, using 3 standard deviations in the formula means that readings at the detection limit are correct within ±33%.
When calculated for tin it shows a detection limit of approximately 8.5 mg/L.  If you recall, the average monthly discharge limit for tin in the state of Rhode Island is 2.00 mg/L. This means that at very low concentrations the results may be skewed. An alternate analytical method may be required in future work to ensure the 2.00 mg/L threshold is met. To minimize the effects of the low detection limit on the rate constant graphs, a larger initial concentration of 160 mg/L was chosen.