On-line version ISSN 0378-4738
Water SA vol.39 n.5 Pretoria Jan. 2013
JB MolwantwaI; PD RoseII, *
IDigby Wells Environmental, Private Bag X10046, Randburg 2125, Johannesburg, South Africa
IIDepartment of Biochemistry, Microbiology and Biotechnology, Rhodes University, Grahamstown, 6140, South Africa
Where sulphate removal is targeted in the biological treatment of acid mine drainage wastewaters, a step additional to sulphate reduction is required to prevent the complete oxidation of sulphide back to sulphate. This linearisation of the biological sulphur cycle has presented a technological bottleneck, particularly in passive treatment operations. We report an investigation of sulphur production in floating sulphur biofilms as a means for addressing this problem. These 50 µm to 500 µm structures may be seen to form on the surface of sulphidic, organic waters and in which sulphide is partly oxidised to So and polysulphide. A Linear Flow Channel Reactor was developed in which the formation of the floating sulphur biofilm could be optimised and studied under controlled conditions. In this study the sulphide feed was sourced from a lignocellulose packed bed reactor treating a synthetic acid mine water (2 000 mg.ℓ-1 Na2SO4 solution) and the Liner Flow Channel Reactors (surface area 1.1 m2 and 2.2 m2) were operated in a controlled environment chamber. The floating sulphur biofilm was harvested by settling to the bottom of the reactor where it remained largely unreacted until removed. It was shown that up to 88% of sulphide in the feed stream may be removed in this way and that this was achieved mainly by oxidation of sulphide to sulphur (including a polysulphide fraction). A mass balance accounting for the process showed that up to 66% of total sulphur species entering the system were recovered as So. Oxidation of sulphide to thiosulphate and sulphate was not found to be significant. A fraction of fine particulate sulphur is released into the stream on harvesting of the biofilm which does not readily settle in the reactor and may thus be lost to the mass balance account. The effects of temperature, loading rate and reactor surface area were investigated in optimising the performance of the reactor. Scale-up application studies in the use of the Linear Flow Channel Reactor in an acid mine drainage passive treatment environment have been undertaken in field studies.
Keywords: floating sulphur biofilms, acid mine drainage, AMD passive treatment, linear flow channel reactor, sulphur biotechnology
Environmental impacts of acid mine drainage (AMD) on public water systems may be widespread and South Africa presents a paradigm case where, following over a century of intensive gold and coal mining operations, water-scarce Witwatersrand and Mpumalanga areas are now under threat (McCarthy, 2011). Both large-volume and diffuse flows require treatment and biological processes offer potential advantages of low cost and low operational input requirements, particularly where applied in passive treatment operations (Molwantwa et al., 2009). The long-term nature of the problem also needs to be considered and, with certain Roman mine workings in Britain and Europe reportedly still actively generating AMD some 2000 years later (Field, 2003), the extended time frames over which the problem will require treatment needs to be taken into account. The sustainability of treatment operations over the long time periods anticipated also favours biological process options (Rose, 2005).
Biological treatment involves the manipulation of the biological sulphur cycle at one or more of its stages of operation, with the reduction of sulphate to sulphide by sulphate-reducing prokaryote (SRP) populations and providing the first unit operation in the process. Apart from neutralisation and metal removal functions, which may be effected at this stage, it is also necessary to remove sulphur from the stream in one of its reduced forms in order to prevent its complete oxidation back to sulphate. However, linearisation of the biological sulphur cycle has presented a technology bottleneck, particularly in the development of passive treatment operations, and a variety of processes have been considered for the effective removal of sulphur (Molwantwa et al., 2009).
Here we report a bioprocess development study on sulphur removal from AMD which is based on its formation in floating sulphur biofilms (FSB). These structures, which are 50 µm to 500 µm thick, form on the surface of sulphidic, organic waters (Fig. 1A), and our initial observation and investigation of FSB structures were reported for tannery wastewater evaporation ponds (Rose et al., 1996; Dunn, 1998). FSB have been shown to be true biofilms in both structural and functional features (Gilfillan 2000; Rein 2002; Bowker, 2002; Rose et al., 2002; Molwantwa et al., 2007). Molwantwa (2008) demonstrated the presence of well-differentiated aerobic, anoxic and anaerobic functional zones within these biofilms in which redox conditions are poised over a narrow range around -150 mV and thereby enable sulphur formation in the polysulphide and orthorhombic So forms (Fig. 2). Where conditions are maintained that allow the biofilm to thicken, it will finally break away from the surface and settle at the bottom of a reactor vessel, where it remains largely unreacted until removed.
Preliminary studies on the use of the FSB system for sulphur removal in Integrated Managed Passive Treatment Systems (IMPI) had demonstrated a potentially robust application for the process under field conditions (Molwantwa et al., 2007). Here it had been located as a unit operation following AMD sulphate reduction in the lignocellulose-based Degrading Packed Bed Reactor (DPBR) described by Coetser et al. (2005). However, under these conditions it had proved difficult to derive operational and kinetic data for purposes of process design and systematic scale-up from the field-scale floating biofilm reactor system first used (Fig. 1B).
Here we report the development of the Liner Flow Channel Reactor (LFCR) in which FSB formation and sulphur removal could be studied under controlled experimental conditions. Process variables investigated included reactor surface area, loading rate of the sulphide stream and the effect of temperature on process operation.
MATERIALS AND METHODS
Shallow rectangular PVC channels (100 mm deep and 150 mm wide) were used for the construction of the reactor vessels (Fig. 1C). These were connected in series in configurations of 4 and also 8 channel units, providing a total surface area of 1.1 m2 and 2.2 m2, respectively. Surface baffles were fitted at the outlet of each channel section and thus constraining the floating film within the channel reactor.
A synthetic mine-water (2 000 mg.ℓ-1 Na2SO4) was prepared using industrial grade sodium sulphate (Protea Chemicals), and then fed to a molasses supplemented 10 m3 DBPR which is a lignocellulose-packed unit developed for AMD passive treatment operations and in which the sulphate reduction reaction is optimised (Coetser et al., 2005).
The LFCR was operated in a controlled environment chamber with operational temperatures set at 15oC (±0.5oC); 20oC (±0.5oC) and 25oC (±0.5oC) for each of the temperatures studied. The DPBR sulphide feed stream to the LFCR was fed at loading rates of 1 309 ℓ.m-2.day-1 and 2 618 ℓ.m-2.day-1.
Operating variables were examined in the LFCR in a series of runs in which the effects on the process of temperature, feed loading rate and reactor surface area were measured. Before each run the reactor was drained and cleaned and then a run commenced with filling of the reactor with sulphide feed from the DPBR. After a period of 24 to 48 h the FSB would establish on the water surface in the reactor and develop through 3 clearly-defined stages of 'thin', 'sticky' and 'brittle' biofilm, as described by Molwantwa (2008). The appearance of polysulphide/So granules in the biofilm has been linked to the appearance of 'brittle' texture biofilm. Once the 'brittle' film had appeared, loading at the desired rate commenced and, in particular, loading rates of 1 309 ℓ.m-2.day-1 and 2 618 ℓ.m-2.day-1 were evaluated. Harvesting of the FSB involved spraying a fine mist of tap water onto the surface of the 'brittle' film which resulted in portions becoming destabilised, breaking away and then settling to the bottom of the reactor channel. This allowed the formation of new 'thin' and 'sticky' film at the surface and, when full coverage with 'brittle' film was complete, the harvesting process was repeated once again. Harvesting was thus undertaken every 12 to 18 h over the time period of the particular run.
Daily analyses of the influent and effluent flows were undertaken for soluble sulphide, sulphate, thiosulphate and sulphur for purposes of mass balance determination. Once a run had been completed the reactor was drained, the sulphur biofilm material which had settled in the reactor channels was collected, dried and weighed, and analysed for sulphur content. A cone settler was located at the LFCR outflow to collect smaller particles that may be carried along with the stream flow. This was also emptied and the sulphur biofilm material collected, dried and added to that recovered from the LFCR. The volume of liquid drained from the reactor and cone settler was also measured and the final analyses used for mass balance determinations as outlined below.
Triplicate samples were drawn for each of the data sets reported and analysed for soluble sulphide, sulphate, thiosulphate, sulphur and pH, Redox potential and COD. Results were averaged and reported as the mean of 3 samples.
The Merck Spectroquant" system was used for soluble sulphide determination (Merck, South Africa). Samples were collected in test tubes containing 100 µℓ of 0.1 M zinc acetate solution. Photometric readings were made using the SQ 118 spectro-photometer (Merck, South Africa).
Sulphate and thiosulphate
Sulphate was determined using ion chromatography in a Waters model 600 HPLC and Waters model 432 conductivity detector (Waters, South Africa) fitted with an IC-PakTM anion 4.6 x 50 mm column (Waters, South Africa). Samples were prepared using a 10-fold dilution of sample in milliQ water and then filtered through a 0.45 |im nylon filter before being passed through 2 Waters Sep-Pak light C18 cartridges (Waters, South Africa) to remove contaminating organic compounds. The system was run at a flow rate of 1 mℓ.min-1 and results analysed using the EMPOWER software programme (Waters, South Africa). A borate/gluconate buffer was used for eluent preparation. All chemicals and filters were from Merck, South Africa. A standard solution containing Fe-, Cl-, NO3-, Br-, HPO42- and SO42- in milliQ water was prepared weekly.
A reverse-phase HPLC method was used for sulphur determination (modified from Mockel 1984). Three 1 mℓ samples were collected, centrifuged for 5 min at 13 000 r.min-1 on an Eppendorf 5415D centrifuge and air dried. After drying, 1 mℓ acetone was added to the pellet and left to stand for 1 h with vigorous shaking every 10 min. The samples were filtered through a 0.45 µm nylon filter (Merck, South Africa) and analysed using the EMPOWER software on a Waters 600 model HPLC and a Waters model 2487 dual λ absorbance detector fitted with a Nova-Pak° C18 3.9 x 150 mm column (Waters, South Africa). The samples were injected and run at 2 mℓ.min-1 using a 5:95 ratio of water:methanol (Merck, South Africa) as the eluent. A 20 mg.ℓ-1 standard solution of elemental sulphur in acetone was used for standardisation.
pH was measured using a model 330 WTW pH/mV meter (Merck, South Africa).
Redox potential was measured using a WTW pH/mV 330 meter (Merck°, South Africa).
Chemical oxygen demand
Chemical oxygen demand (COD) was determined using the digestion and titration method (APHA, 2005).
Floating sulphur biofilm
After each reactor run settled FSB material was collected and dried at 80oC for 5 days.
Mass balances were calculated to provide an account for influent, effluent and recovered sulphur species calculated as S, as shown in the process train (Fig. 3).
The percentage mass balance recovery was calculated as follows:
Total sulphur species IN = Total sulphur species OUT + Total sulphur recovered
(So+So42-+HS-+S2O3-)IN = (So+SO42-+HS-+S2O3-) OUT + (So+SO42-+HS-+S2O3-) RECOVERED
Mass balance loss (%) = [(SIN -SOUT) + (S RECOVERED) / SIN] * 100
Mass balance recovery (%) = 100 - Mass balance loss (%)
Sulphide removal (%) = [(Sulphide IN - Sulphide OUT)/ Sulphide IN]*100
Sulphur recovery (%) = [(Sulphur OUT - Sulphur IN)/ Sulphide IN]*100
Statistical evaluation of data sets was undertaken using Statistica data analysis software Version 7.1 (StatSoft, Inc.).
RESULTS AND DISCUSSION
The effect of temperature on process performance was evaluated at 15oC, 20oC and 25oC. In each case, operation of the experimental 4-channel LFCR (1.1 m2) was repeated over a number of 18-day runs and then 8-day runs from which the data reported here were collected. A loading rate of 1 309 ℓ.m-2.day-1 of sulphide-enriched synthetic AMD from the DPBR was applied to the LFCR in these runs.
A mass balance for each run was determined (as described above) in order to account for the passage of all sulphur species (as S) passing through the system. Results are reported in Table 1.
Of total sulphide fed to the LFCR, 74% was removed with the operation at 20oC. Sulphide removal was reduced at both the lower and the higher operating temperatures with removal of 53% at 15oC and 39% at 25oC. The recovery of elemental sulphur S (including polysulphide) ranged between 28% and 43% of total sulphur species fed to the reactor during the temperature runs (Table 1). Figure 4 shows no significant increase in thiosulphate or sulphate concentration in the effluent over the influent stream (p=0.48 and p=0.36 for thiosulphate and sulphate, respectively), which indicates that the unaccounted fraction of sulphur was not primarily due to the near-complete or complete oxidation of influent sulphide. The pH in the reactor rose to between pH 8 and 8.4 (Fig. 5) which suggests limited losses due to sulphide stripping into the air, except possibly in the influent before pH elevation. A component of fine particulate sulphur may be released from the FSB during harvesting when the 'brittle' film breaks up and settles to the bottom of the reactor. This fine particulate fraction does not settle readily in either the channels or in the cone settler and may account, in some part, for the discrepancy between sulphide removal and the total sulphur mass balance account.
The results in Fig. 5 were typical for all runs and, in addition to pH, show redox and COD profiles during runs. An elevation in redox potential from around -230 mV in the influent to -155 mV in the effluent is important given that the oxidation of sulphide to elemental sulphur, rather than to more oxidised states, occurs in a narrow redox window around -150 mV (Steudel, 1996). The influent COD was reduced by approximately 200 mg.ℓ-1 during the course of flow through the reactor. This suggests that some reduction of sulphates may have occurred in anaerobic zones within the reactor channels. Since heterotrophic consumption of COD by both sulphate-reducing and non-sulphate reducing organisms is likely to have been involved, the component due to sulphate reduction alone could not be quantified in the current study. However, this may need to be taken into account in a more detailed determination of actual sulphide removal achieved in the system.
These results showed that sulphide removal in the LFCR would be expected to be sensitive to seasonal temperature changes. Interestingly, reduced performance would be more pronounced in warmer summer conditions compared to colder winter conditions. This may be controlled for by altering the feed loading rate and/or the reactor surface area, and subsequent studies on the effect of these variables are reported for reactor runs at the 20°C optimum operational temperature demonstrated here.
The effect of loading rate on the performance of the LFCR was evaluated by comparing its operation at 1 309 ℓ.m-2.day-1 and 2 618 ℓ.m-2.day-1 loading rates at 20ºC.
The results of the loading rate studies are shown in Fig. 4 (1 309 ℓ.m-2.day-1) and Fig. 6 (2 618 ℓ.m-2.day-1) and are summarised in Table 2. In both loading rate studies the removal of sulphide at 62% for the lower loading rate and 74% for the higher loading rate was found to be significant (p<0.05) and highly significant (p<0.0001), respectively. The higher the flow rate the better the removal of sulphide observed, with an improvement of around 12% observed in this study. This difference was also significant (p<0.05).
However, the recovery of sulphur in the form of biofilm harvested was reduced by 17% at the higher loading rate (60% sulphur recovery at the lower loading and 42% sulphur recovery at the higher loading rate). Indeed, the difference in the sulphur content between the influent and effluent streams was not significant (p=0.48) at the higher loading. This result strengthens the suggestion that the loss of sulphur in each case may be due to fine sulphur particulates that do not settle and are washed out of the system.
In both loading rate studies the difference between influent and effluent thiosulphate and sulphate concentrations was found not to be significant, once again indicating that the sulphide loss was not primarily due to oxidation reactions within the reactor. The reduced likelihood of sulphide stripping as a possible explanation has been noted above although some losses via this route cannot be excluded.
The effect of reactor surface area on the sulphide removal operation in the LFCR was evaluated by doubling the 4-channel reactor area with the addition of another 4 channels. The 8-channel reactor (2.1 m2) was operated at the 2 618 ℓ.m-2.day-1 loading rate. Results of this study are shown in Figs. 5 and 7 and summarised in Table 3.
With the increase in surface area, 88% sulphide removal was measured which was 14% better than measured in the 4-channel reactor operated at the same loading rate, and 26% better than in the 4-channel reactor operated at half the loading rate. Sulphur recovery at 66% showed an improvement of 23% for the 8-channel reactor compared to the 4-channel reactor at the 2 618 ℓ.m-2.day-1 loading rate, but was more or less comparable to that observed in the reactor operated at the lower loading rate. Once again the difference between influent and effluent thiosulphate and sulphate concentrations was not significant (p=0.48 and p=0.52 respectively), indicating that near-complete or complete oxidation of sulphide does not provide an explanation for the major fraction of unaccounted sulphur in the system.
The results of the study reported here have shown the following: The LFCR offers a relatively simple system for sulphide removal following sulphate reduction in passive treatment operations such as those managed in DPBR units handling AMD flows. Sulphide removal of up to 88% may be achieved in the system and with sulphur recovery of around 60% in the form of polysulphide and So granules.
The process is temperature sensitive and process design will need to take into account losses to be expected in both hot and cold climatic conditions.
The process is responsive to both loading rate and reactor surface area but, within the context of this study, it was observed that higher loading rates and larger reactor surface areas were both associated with higher sulphide removal in the treatment stream.
Total S removal in the AMD feed stream in the LFCR system will require control of the fine particulate sulphur fraction generated in the process and improvement of the separation function requires further study.
While the initial potential of the process has been demonstrated, further refinement of kinetic data is required to improve design inputs required for effective scale-up of the process. Initial studies in this regard have been reported by Van Hille et al. (2011).
Potential has been demonstrated in this study for the scale-up evaluation of the system for use in field-scale passive treatment operations. Such studies have commenced and preliminary results of findings have been reported by Mack et al. (2009).
The authors would like to thank Rhodes University, the Environmental Biotechnology Research Unit and the Water Research Commission for funding Project K5/1454 and for permission to use data from WRC Report No. TT 411/09.
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Received 30 July 2012
Accepted in revised form 23 September 2013