Abstract

In drinking water treatment plants, chemical reagents are employed to aggregate and remove suspended particles. However, not all reagents are eco-friendly and exists concerns over environmental, economic, and health issues. This study shows features of the sustainability of commercial coagulants/flocculants and presents experimental research on floc characterization and settling of dispersed solids with a combination of Ferric Chloride (FeCl₃ ) and gelatinized starch. Bench studies were conducted using kaolin suspensions and results were validated with raw water collected from a river (Rio dos Sinos, Brazil). Flocculation indexes, floc structure, and residual turbidities were compared with Polyaluminum Chloride (PAC), as a reference. All techniques showed that the combination of FeCl₃ and starch formed well-structured, larger, and more settleable flocs than those produced with PAC. Superficial loadings, in a continuous separation tank (2 to 4 m.h^-1) were studied with and without lamellae. Best results were obtained with 15 mg.L^-1 Fe³⁺ and 10 mg.L^-1 starch, with a velocity gradient, G, of 60 s^-1 in the slow mixing and with 60° inclined lamellae spaced 1.3 cm apart. Best conditions were applied to the clarification of the raw water and again, due to the rapid settling of flocs with FeCl₃ and starch, better results were obtained compared to PAC. A turbidity reduction of 94% and a residual value of 2.5 NTU with superficial loadings of 3 m.h^-1 were obtained. Results were discussed in terms of interfacial and operating parameters and a promising potential for the combination of FeCl₃ with starch for solid/liquid separation was envisaged.

Keywords

Drinking water treatment; Reagent sustainability; Coagulation-flocculation-settling; Iron chloride plus starch

Introduction

The effective removal of suspended solids (micro and nanoparticles) is fundamental in drinking water treatment, reducing turbidity, odor, color, and organic matter from raw water. Thus, the efficient aggregation (coagulation and/or flocculation) and settling (or flotation) of the dispersed particles is key and attention has to be drawn to the selection of a suitable and sustainable destabilizing reagent [1-3].

According to BCC Research (2020), the global market of reagents for water and wastewater treatment will grow to more than $111 billion by 2024, at a Compound Annual Growth Rate (CAGR) of 3.2%. Yet, because this market includes reagents that might cause some environmental and public health problems, there is a general trend in the search (and research) for eco-friendly coagulants or flocculants that reduce these risks [1,2].

The most common coagulant reagents employed in drinking water treatment plants are those based on aluminum, such as Aluminum Sulfate (Al₂(SO)₄) and Polyaluminum Chloride (PAC). Also, Polyacrylamides are occasionally used (at least in Brazil), when the waters are very turbid, as ancillary aggregation reagents assisting the coagulants to improve particle settling velocity [3-5]. Further, tanninbased destabilizing reagents, mostly produced from tree tissues (leaves, wood, or bark), have also been employed in drinking water and industrial effluent treatment units. These compounds adsorb onto the particles surfaces by a combination of electrostatic attraction, hydrogen bonding, and/or polymeric bridges, which depend on their charge density, molecular weight, and branching [6-8].

Environmental considerations

There is a major concern in the international scientific community about the safety of some of these reagents, especially those containing aluminum. There has been an ongoing discussion on the relationship between this metallic element (even at low concentrations) and neurodegenerative diseases [9-12].

In most countries, emission standards have been established for the total aluminum (Al³⁺ and Al(OH)₃) in treated water. Thus, the World Health Organization recommendation is 0.2 mg.L^-1 [13,14] as in Brazil (Ministry of Health, 2017) and Germany [15]. In the USA values vary between 0.05 and 0.4 mg.L^-1, depending on the state [12], while in Canada, the standards vary between 0.1 and 0.2 mg.L^-1 [16]. These levels are general references and there is a worldwide consensus towards reducing these values to decrease the total intake of this metal [11].

Healthy individuals readily eliminate the residual aluminum present in treated water whereas elderly people with liver and kidney problems might accumulate it [9-12,16]. This situation may be aggravated considering daily higher exposure to this element via food, antacids, and cosmetics.

Regarding synthetic polymer flocculants, these chemicals usually release residual monomers, formed during polymerization synthesis. These compounds are remarkably toxic to humans, animals, and aquatic organisms [17,18].

Moreover, the manufacturers of polyacrylamides are reluctant to divulge the exact chemical composition of their products. Despite that, it is known all are based on acrylamide chemistry and might present risks due to the toxicity of the by-products through polymerization reactions, notably acrylamide. Thus, degradation and transfer of the monomers to either surface or underground water courses is also a problem for aquatic species [17,18].

In Brazil, the acrylamide limit in drinking water is 0.5 µg.L^-1 as regulated by the Ministry of Health (Portaria de Consolidação MS 05/2017, Annex XX). The European Union has set a more restrictive parametric value for human tap water consumption at 0.10 µg.L^-1 acrylamide [19]. According to the World Health Organization [13], values of about 0.5 µg.L^-1 may serve as a guideline, but recommend that the exposure should be reduced to a level as low as technically achievable.

Tannin-based flocculants commercialized as organic and natural products in water treatment are modified natural tannins (predominantly from the bark of the tree Acacia mearnsii) with formaldehyde (classified as a category B1carcinogen) and ammonium chloride during the Mannich reaction [8,20]. As a result, the tannins are converted into a cationic form [8,21,22]. Recently, Machado G, et al. [8] studied the production of tannin-based flocculants without the need of using formaldehyde. The novel synthesis technique of a friendlier reagent appears to have good potential in terms of color and turbidity removal from simulated water.

To summarize, many international standards are starting to regulate the commercial products employed in water treatment, establishing sampling and analysis rules, as well as listing minimum health requirements. The focus is primarily on the associated chemical, either contaminants or impurities, which might end up in treated water [23]. Further, manufacturers should ensure the stability and sustainability of their commercial products by attending to these regulations and carrying out regular chemical analyses.

Alternatively, the development of eco-friendly coagulants/ flocculants is being studied, namely, applications involving natural starches and derivatives. Interestingly, gelatinized starches have been used heavily since the early 20^th century as flocculants in many industries, principally in mineral (iron ore) processing [24,25]. Lately, these reagents have been rediscovered for applications in effluent and water treatment [26-28].

The main advantages of natural-based flocculants, compared to the synthetics, include the availability of the raw material, the low levels of toxicity and corrosion, as well as the lower volume of sludge generated and biodegradability [2,28,29].

Yet, some of the natural-based aggregation reagents, such as starch, chitosan, cellulose, guar gum, and dextran are modified and/ or incorporated (grafted) with many chemical compounds aimed at enhancing their coagulation/flocculation properties [2]. These modifications include copolymerization of the natural molecule with acrylamide, or other monomers, to generate grafted hybrid structures. Reactions with organic ammonium salts, mercaptans, sulfonic acids, carbamates, acrylates, among others, are conducted to modify their molecular weight, functional groups, and charge density characteristics. Again, concern and caution with respect to their chemical modifications should always be taken into account.

Examples of water and wastewater treatment studies using untreated starch-based flocculants are shown in table 1.

Reagents	Conditions	Main results	References
Al2(SO4)3+cassava peel starch	AMD, acid mine drainage water treatment	89% reduction in suspended solids and >80% Escherichia coli	[30]
Al2(SO4)3+gelatinized rice starch	Effluent of palm oil production treatment	Reduction of 88% TSS, 27% COD, 44% total phosphorous, and 42% total nitrogen	[31]
FeCl3 and gelatinized corn starch	Titanium dioxide nanoparticles (TiO2-NPS) removal by flocculation and settling or flotation	99% TiO2-NPs removal (residual concentration <30 mg.L-1)	[27]
Al2(SO4)3, chitosan, sodium alginate, potato starch	Supply water treatment	74-80% color removal	[28]
FeCl3 and gelatinized corn starch	Treatment of turbid surface water	90 and 100% reduction in turbidity	[26]

Table 1: Main studies of untreated (non-modified) starches used in the treatment of water and effluents by coagulation-sedimentation.

The main objective of this work was to evaluate the combination of ferric chloride and gelatinized natural starch an eco-friendlier alternative for drinking water treatment, especially when compared with the Polyaluminum Chloride (PAC). Herein, the flocculation index and the removal of dispersed solids from simulated water were fully studied. Best results were applied in real raw water in a continuous lab scale (Rio dos Sinos, Brazil) and the comparative effect of those reagents on the hydraulic superficial loading capacity was also studied.

Experimental

Materials

In the bench batch studies, Deionized (DI) water with pH=5.5 and conductivity < 4 µS.cm^-1 was employed with public water (Porto AlegreBrazil) in a continuous system. The simulated raw water was prepared with fine kaolin particles (D32=22 µm, D10=3.5 µm, D50=17.3 µm, D90=36.3 µm).

Polyaluminum Chloride (PAC Floc H120 HT-Ambientaly Ind., Brazil) and Ferric Chloride (FeCl₃.6H₂ O-Dinâmica Química, Brazil) were the coagulation reagents. Sodium hydroxide (NaOH-Dinâmica Química, Brazil) was used to adjust the pH.

Commercial corn starch (Maizena^®, Unilever, Brazil) was used in the bench tests and high purity corn starch (Starch P.A.-Dinâmica Química, Brazil) in the continuous studies. The gelatinized starch was made from a mixture of 10 g starch and 1 g NaOH in 1 L of DI water at 65°C until a homogenous gel was obtained.

The raw water was collected from the Rio dos Sinos at the COMUSA Water Treatment Plant (WTP) (Novo Hamburgo, Brazil) and had a turbidity of 26.2 NTU, electrical conductivity of 89 µS.cm^-1, and a pH of 6.5.

Methods

Bench-scale studies: This stage aimed to optimize the physicalchemical and hydrodynamic parameters of aggregation: pH, coagulant concentration, and velocity Gradients (G). A jar test (Nova Ética^®, model 218-3LDBF, Brazil) was employed and the tests were conducted with 120s of rapid mixing (G=1000 s^-1) followed by 300s of slow mixing (G=40 s^-1, 60 s^-1, 80 s^-1 and 100 s^-1) and a separation time of 300s. The turbidity of the simulated raw water and treated water were measured in a bench turbidimeter (HACH^®, 2100 N).

The coagulation-flocculation was studied under the following conditions: i) PAC (40-70 mg.L^-1); ii) FeCl3 (5-20 mg L^-1 of Fe³⁺) and gelatinized starch (0-15 mg.L^-1) [30,31].

Herein, the ferric-based coagulant used was FeCl₃ (Ferric Chloride) and the concentrations are expressed in mg.L^-1 of ferric ion (Fe³⁺). All these terms are used indistinctly throughout the text.

In the experiments with FeCl₃ plus starch, the ferric coagulant and the starch were added during a rapid mixing stage for 1 min and finally, the slow mixing was conducted for 5 min. With PAC, the addition was done in two instances: the first dose (30-60 mg.L^-1) during the rapid mixing stage and the second (10 mg.L^-1), added at the beginning of slow mixing, for floc growth.

Particle aggregation studies: The aggregation status of the suspended particles was measured in a photometric dispersion analyzer (Rank Brothers^®, Photometric Dispersion Analyzer-PDA 2000) described in figure 1. This equipment uses a laser beam and an optical sensor that converts the transmitted light signal (related to the turbidity of the sample) and a floating signal (related to random variations in the number of particles) into an output Voltage (V) that indicates the sample’s Flocculation Index (FI) [6,32].

Figure 1: Schematic illustration of dispersion Photometric Analyzer (PDA). A) Peristaltic pump with a modular controller; B) 1 L cylindrical reactor with coupled mixer and pH probe; C) PDA reader; D) Data recorder; E) Notebook.

Evaluation of sludge volume and floc structure: A microscope (BEL Photonics®, bulb 12V 20W, WF10X) was used to capture microphotographs of the flocs formed (best aggregation condition). The sludge generated after 1 h was examined in an Imhoff cone (J Prolab^® ), following the standard methods for the examination of water and wastewater (2540 F-Settleable Solids) [33].

Continuous water treatment studies: The effect of the superficial hydraulic loading (m.h^-1) was evaluated using Conventional (SC) or Lamellar (SL) settling to remove the suspended solids from the treated simulated effluent. The continuous unit is described in figure 2 and the design (dimensional) parameters are shown in table 2.

Figure 2: Continuous water treatment system by flocculation-settling: A: Feed water and coagulation tank; B: pH meter; C: Peristaltic pump; D: Flow meter; E: Flocculation units (1=Fast mixing, 2=Slow mixing); F: Dosing pumps; G: Separation (settling) unit; H: Sludge drain; I: Outlet of the treated water.

	Coagulation	Flocculation (rapid mixing)	Flocculation (slow mixing)	Settling
Dimensions (cm)	Ø=57.5/ h=104	L=12/W=29/ h=25	L=25.5/ W=29/h=25	L=51/ w=13.5/h=25
Volume (L)	250	7.3	15.5	15.8
Detention time (min)	54.3-107.3	1.6-3.1	3.4-6.6	3.4-6.8

Table 2: Design (dimension) parameters of the continuous effluent (water) treatment system. Physical dimensions: Ø=diameter, h=height, W=width, L=length.

The waters to be treated (kaolin suspension or raw water) were transferred to the separation unit with a peristaltic pump. The pH was adjusted with NaOH and the flocculants were added with dosing pumps (Exxata^® EX1) at the inlet of the flocculation chamber (rapid mixing).

The lamellae inserted in the settling tank are 32 acrylic plates (11.5 cm × 7 cm) spaced 1.3 cm apart and inclined at an angle of 60° (best results). The residual turbidity (duplicates), were monitored in samples (20 mL) at 5 min intervals. The experiments were conducted after a stabilization time of 30 min (steady-state regime), equivalent to 2 residence times of the effluent during flocculation and sedimentation.

The continuous studies of kaolin/water separation by coagulationflocculation-settling were validated with raw water, collected from Rio dos Sinos, Brazil.

Results and Discussion

The main industrial application of starch is the reverse cationic flotation of gangue particles in mineral processing which act as a flocculant-depressant for the flotation of iron-bearing mineral particles. Here, the gelatinized starch flocculates the iron-bearing particles selectively, permitting the flotation of the siliceous gangue particles, with amines as a collector [24,34].

Authors explain that this selectivity is due to the chemical adsorption of the starch composite onto the iron-bearing species, mainly oxides and hydroxides [24,25]. The idea of using the combination of FeCl₃ and gelatinized starch herein, a non-toxic coagulant-flocculant mixture, in water treatment, came from this industrial observation.

Studies to improve the flocculation ability of starches have followed different directions, namely: i) Gelatinization of the natural starches to free the amylose and amylopectin molecular fractions; ii) Modifying the starch structure chemically, mostly to convert them into cationic flocculants [2,34-36] and iii) Combining the starches with common coagulants, such as aluminum sulfate or ferric chloride. The last was the alternative studied in this work, following the viewpoint that the chemical modification of the starches must be well controlled and accepted by the environmental and sanitary agencies [2,8].

Bench studies

Particle aggregation studies by photometric dispersion analysis: Figure 3 shows the flocculation index (FI values) of kaolin particle suspensions as a function of time, comparing values obtained with PAC (30-60 mg.L^-1) to those with varying starch concentrations (5-15 mg.L^-1) while keeping Fe³⁺ concentration constant at 10 mg.L^-1. Results showed optimal values (FI on the order of 5) at 10 mg.L^-1 of starch, and rapidly decreasing at lower and higher dosages. Contrarily, FI values with PAC were all very low and these results may be explained in terms of the larger and stronger flocs formed by the combination of ferric chloride and starch, compared with PAC (Figure 4).

Figure 3: Flocculation index of aqueous kaolin suspensions as a function of time at various concentrations of starch or PAC. Conditions: [Fe³⁺]=10 mg.L^-1 (for the experiments with starch); pH=7; Feed turbidity=45 NTU; [kaolin]=0.13 g.L^-1; G=40 s^-1 (PAC) and 60 s^-1 (Fe³⁺+starch).

Figure 4: Microphotographs (1280 × 1024 pixels) of the flocs under two different conditions: a) 10 mg.L^-1 Fe³⁺+10 mg.L^-1 gelatinized starch, pH=7 and G=60 s^-1 (5 min); b) 60 mg.L^-1 PAC, pH=7 and G=40 s^-1 (5 min).

Besides, Duan and Gregory (2003) reported that when using very high PAC dosages, the particles may become positively charged and that charge reversal could re-stabilize the particles, resulting in a loss of aggregation efficiency.

Characterization of flocs and settled solids: The microphotographs show that with FeCl₃ and starch, flocs are more compact and denser than those formed by PAC (Figure 4). See other photographs in the Supplementary Data (Figure S1-S6).

Table 3 shows the results of the sludge volumetric concentrations in an Imhoff cone, comparing Fe³⁺ plus starch tothe flocs formed with PAC. Supplementary data (Figure S5) shows photographs of the Imhoff cone assays. After 5 min of slow mixing and 1 min of settling, the flocs formed with ferric coagulant and starch had a volumetric concentration of sludge at 10 mL.L^-1, while the flocs formed with PAC needed almost 40 min to obtain this very same value. These results match the Flocculation Indexes (FI), obtained by Photometric Dispersion Analysis (PDA), and reveal higher settling kinetics, which is very important in the design of water treatment plants, with a lower footprint. Again, these results are probably due to the denser structure of the flocs generated by ferric chloride plus starch.

	Volume (mL.L-1)
Time (min)	PAC	Fe3++Starch
5	0	10
20	5	12
40	12	13
60	14	14

Table 3: Comparative settled solids volumetric concentrations in an Imhoff cone as a function of time. Conditions: same as figure 4.

Comparative flocculation-settling of kaolin particles: Figure 5 shows the residual turbidity in the treated water as a function of the concentrations of ferric ion (starch concentration kept constant at 10 mg.L^-1) with two feed turbidities. Best results were obtained (about 1 NTU or 99% removal) between 10-15 mg.L^-1 Fe³⁺ and with the higher feed turbidity (130 NTU), at pH=7. These results of flocculationseparation of the kaolin particles are explained by the following mechanisms:

Figure 5: Coagulation-flocculation-settling of kaolin aqueous dispersions. Residual turbidity as a function of the concentration of Fe³⁺ and feed turbidity (45 and 130 NTU or 0.13 and 0.22 g.L^-1 of kaolin, respectively). Conditions: [Starch]=10 mg.L^-1;G= 1000 s^-1 (2 min, rapid mixing); G=40 s^-1 (5 min, slow mixing); settling time=5 min and pH=7.

i. Firstly, rapid adsorption of the starch by a chemical interaction between the amylopectin fraction and the iron present at the surface of the Fe(OH)₃ precipitates or flocs [26,27] and,

ii. Entrainment or sweeping of the kaolin suspended particles by the flocs as a carrier. The higher the feed turbidity, the more effective is this separation by coagulation-flocculation-settling of kaolin aqueous dispersions.

Figure 6 shows the residual turbidity in the treated water as a function of the concentrations of PAC with a feed turbidity of 45 NTU. The best results (residual turbidity of 1 NTU, 98% removal) were obtained with 60 mg.L^-1 of PAC, employing the same hydrodynamic conditions as those with the iron-starch flocculant (G=40 s^-1 and 5 min). The turbidity removal was similar to that with Fe³⁺ and starch, obtained at a higher concentration.

Figure 6: Coagulation-flocculation-settling of kaolin aqueous dispersions at bench scale (jar-test) as a function of the concentration of PAC. Conditions: feed turbidity=45 NTU (0.13 g.L^-1 of kaolin); G=1000 s^-1 (2 min, rapid mixing); G=40 s^-1 (5 min, slow mixing); settling time=5 min and pH=7.5.

As shown in figure 7, increasing the velocity gradient (G, s^-1) in the slow mixing, from 40 to 100 s^-1, with 10 mg.L^-1 of Fe³⁺ plus 7.5 mg.L^-1 of starch, gave better results with a removal >99% of feed turbidity or residual turbidity of 0.3 NTU (triplicate tests) in the final treated water. Conversely, with PAC, these results were unstable (high standard deviation) and poorer at a velocity gradient higher than 40 s^-1 in the slow mixing because the formed flocs were fragile and do not withstand the shear forces. As a result, some of the aggregates were broken and had lower settling velocities and higher residual turbidities. The supplementary data (S) presents further data (effect of pH and starch concentration).

Figure 7: Coagulation-flocculation-settling of kaolin aqueous dispersions at bench scale (jar-test) as a function of the velocity gradient (G), with FeCl₃ plus starch or PAC. Conditions: Feed turbidity=45 NTU (0.13 g.L^-1 of kaolin); [Fe³⁺]=10 mg.L^-1; [starch]=7.5 mg.L^-1; PAC=60 mg.L^-1.

Coagulation-flocculation-settling studies in a continuous system:

Kaolin suspensions: Figure 8 shows that residual turbidity in the treated water increased as a function of superficial loading by values upto 4 m.h^-1, independent of the reagent used. These results are due to the higher flow velocity (water displacement) and shorter residence time in the separation unit, dragging the flocs towards the treated water outlet. Because of the more turbulent conditions at higher superficial hydraulic loading, some breakage of flocs may occur, decreasing the aggregate settling, keeping them suspended in the treated water.

Figure 8: Coagulation-flocculation-settling of kaolin suspended particles in a continuous system.
Residual turbidity (NTU) as a function of the superficial loading, with lamellar settling (LS) and without lamellae. Conditions: Feed turbidity=48 NTU (0.15 g.L^-1 kaolin); 15 mg.L^-1 of Fe³⁺+10 mg.L^-1 of starch; pH=7; G slow mixing=60 s^-1 (starch); PAC=60 mg.L^-1; pH=7.5; G slow mixing=40 s^-1 (PAC).

The presence of inclined lamellae reduced the residual turbidity in the treated water, due to the lower turbulence in the space between the plates, thus eliminating unstablqe flows and mixing currents. The sloping surfaces of the plates reduce the distance particles need to settle in the bulk suspension, agglomerating and sliding down when they reach the surface of the plates [37-39].

As discussed earlier, the bigger and stronger flocs formed with Fe³⁺ and starch withstands more shear than those formed with PAC (Figure S6). The faster settling and higher resistance to the shear forces allowed enhancement of the superficial loading in the case of flocculation with starch, reaching values of 3 m.h^-1, keeping the average residual turbidity around 5.6 NTU.

Public supply raw water: Figure 9 shows excellent results with the combination of Fe³⁺ plus starch when compared with PAC. The residual turbidity of 2.5 NTU, equivalent to a reduction of 90%, was attained at a superficial loading of 3 m.h^-1 using lamellar settling at a higher velocity gradient (G values, 40 s^-1 with PAC and 60 s^-1 with Fe³⁺+starch).

Figure 9: Treatment of raw water from Rio dos Sinos, Brazil in a continuous system of coagulation-flocculation-lamellar settling, using two types of aggregation reagents. Comparison of residual turbidity at a superficial hydraulic loading of 3 m.h^-1. Conditions: initial turbidity=26 NTU; 15 mg.L^-1 Fe³⁺+10 mg.L^-1 starch; 60 mg.L^-1 PAC; pH=7; G=40 s^-1 (PAC) and 60 s^-1 (Fe³⁺+starch).

With a lamellar settling regime, the particles appear to change the floc morphology within the lamellae and, once they have exited these plates, they are not drawn into the treated water liquid flow [39].

The supplementary data (Figures S2 and S3) shows video data of the floc settling and hydrodynamics between the lamellae plates.

These results are considered the most important in this work, because they not only validate the bench and continuous data obtained with kaolin suspensions but also proved higher efficiency showing that with iron chloride and natural starch, higher process (settling) velocities can be obtained. The superficial loading capacity attained is higher than that currently applied at the drinking water treatment plant of COMUSA, which is 2.5 m.h^-1. This enhanced kinetics may bring advantages such as higher loading capacities in settling units with a lower footprint. This research will continue in pilot runs before industrial trials.

Figure S1: Coagulation-flocculation-settling of kaolin aqueous dispersions at bench scale (jar-test), as a function of pH. Conditions: feed turbidity=50 NTU (0.15 g.L^-1 of kaolin); [Fe³⁺]=10 mg.L^-1; G=1000s^-1 (2 min, rapid mixing); [starch]=10 mg.L^-1; G= 50s^-1 (5 min, slow mixing); settling time=5 min.

Figure S2: Coagulation-flocculation-settling of kaolin aqueous dispersions at bench scale (jar-test) as a function of the concentration of starch. Conditions: feed turbidity =50 NTU (0.15 g.L^-1 of kaolin); [Fe³⁺]=10 mg.L^-1; G=1000s^-1 (2 min, rapid mixing); G=70s^-1 (5 min, slow mixing); settling time=5min and pH=7.

Figure S3: Coagulation-flocculation of raw water (Rio dos Sinos, Brazil) at bench scale. Microphotographs (1280 × 1024 pixels) of flocs formed with Fe³⁺+starch. Conditions: Feed turbidity=33.2 NTU; 15 mg.L^-1 Fe³⁺+10 mg.L^-1; rapid mixing G of 1000 s^-1/2 min; slow mixing G=60 s^-1/5min and pH=7.

Figure S4: Coagulation-flocculation of raw water (Rio dos Sinos, Brazil) at bench scale. Microphotographs (1280 × 1024 pixels) of flocs formed with PAC. Conditions: Feed turbidity=33.2 NTU; 60 mg.L-^-1 of PAC; rapid mixing (PAC)=G of 1000 s^-1/2 min; slow mixing G=40 s^-1/5 min and pH=7.

Figure S5: Imhoff cone assays for the characterization of the volume of settled flocs, with PAC (60 mg.L^-1) and Fe³⁺ plus starch (15 mg.L^-1+10 mg.L^-1).

Figure S6: Kaolin flocs settling in the continuous system. a) Fe³⁺ (15 mg.L^-1)+starch (10 mg.L^-1), pH=7, G slow mixing=60s^-1; b) PAC (60 mg.L^-1), pH=7.5, G slow mixing=40s^-1. Both conditions with initial turbidity=48 NTU (0.15 g.L^-1 of kaolin) and superficial loading=2 m.h^-1.
Full video link: https://youtu.be/jMeebuEgeSE

Conclusions

This work shows features on the sustainability of commercial coagulants/flocculants and presents studies on the use of iron chloride and natural starch for coagulation and flocculation in drinking water treatment at bench and continuous scales. Environmental and sanitary (health) aspects of aluminum-based coagulants, polyacrylamides, and tannin reagents were discussed. Experimental results show that a combination of ferric chloride and starch generated well-structured flocs of kaolin (employed as a dispersion model), forming compacted and larger units than those with polyaluminum chloride (PAC), which led to rapid settling. Continuous studies of lamellar settling validated results treating real raw water (Rio dos Sinos, Brazil) and compared the combination of FeCl₃ plus starch with PAC. Because of the rapid settling and higher strength of the flocs formed, best results were obtained with FeCl₃ +starch, with a higher velocity gradient (G, 60 s^-1) during slow mixing and with a separation tank with inclined lamellae. The higher turbidity reduction (94%) with a residual turbidity of 2.5 NTU obtained at a superficial loading of 3 m.h^-1, compared to 58% of turbidity reduction with PAC (residual turbidity of 11 NTU), appears to show a good potential of the combination of FeCl₃ and starch for solid/liquid separation, especially in drinking water treatment. All results were discussed in terms of interfacial mechanisms involved and operating parameters.

Acknowledgments

The authors would like to thank all the Brazilian Institutions that supported this study, namely: Comusa-Novo Hamburgo, CNPq (Grant number 421284/2018-8), and UFRGS (EE-FLE-PPGE3M). We would like to give special thanks, for their assistance, to all students of our laboratory-LTM, our technician Alex Rodrigues, friends and former students, Dr. Katia Wilberg and Dr. Ramiro Etchepare.

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Article Information

Article Type: RESEARCH ARTICLE

Citation: Gomes CEP, Oliveira HA, Azevedo AC, Rubio J (2021) On the Use of Iron Chloride and Starch for Clarification in Drinking Water Treatment. Int J Water Wastewater Treat 7(1): dx.doi.org/10.16966/2381-5299.178

Copyright: © 2021 Gomes CEP, et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.

Publication history: 

Received date: 28 May, 2021

Accepted date: 17 Jun, 2021

Published date: 24 Jun, 2021