Author: Lukhele, L P; Krause, R W M; Mamba, B B; Momba, M N B
Date published: July 1, 2010
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Safe drinking water is one of mankind's most basic needs. The South African Constitution defines access to safe drinking water as a basic human right; therefore we cannot overemphasize the importance of access to safe drinking water for humans. Safe drinking water is defined as water that does not pose a health risk to consumers (Momba and Brouckaert, 2005). The World Health Organisation (WHO) defines safe drinking water as water that has chemical, microbial and physical characteristics that comply with both WHO and national standards. Bacterial contamination of water is a public health concern because it causes numerous diseases and some aesthetic problems such as malodour in water. Organisms such as Escherichia coli, Shigella spp., Salmonella spp., Vibrio spp., and Cryptosporidium are known to be transmitted by water and cause ill health in communities consuming water contaminated by bacteria.
Water treatment methods currently employed in South Africa have their drawbacks. Chlorine is the most widely used disinfectant (Genthe and Kfir, 1995), but chlorine reacts with water to form hypochlorous acid which in turn can react with natural organic matter (NOM) such as humic acid and fulvic acid to form disinfection by-products (DBPs). These byproducts include trihalomethanes (THMs), polychlorinated biphenyls (PCBs) and other halogenated hydrocarbons (Genthe and Kfir, 1995). Some of these halo-hydrocarbons are known carcinogens and endocrine disruptors and are difficult to remove from water. Also, the detection of organics, microorganisms and other pollutants in distribution systems have proven that there is a need for the introduction of better water treatment methods that will ensure that water supplied to communities is of high quality (Schutte and Focke, 2007).
Silver has a long history of use in medicine as antimicrobial agents (Yoon et al., 2007). Ancient Egyptians used silver vessels to keep wine, water and vinegar for purification (Shashikala et al., 2007). The antimicrobial activity of silver ions involves their interaction with the -SH group in bacterial enzymes (Wilks et al., 2005) and produces structural changes to the cell membranes of bacteria (Alcamo, 2001). Studies conducted on bacterial cells exposed to silver showed cell damage consistent with cell membrane damage (Brook et al., 2007). Silver deposited on carbon surfaces has been proven to have strong antibacterial action. Electrodeposited silver on activated carbon was shown to reduce viable bacteria in water by up to 7 log (Ibarra et al., 2007).
Carbon nanotubes and cyclodextrin polymers synthesised in our laboratories have the capability to remove organic pollutants from water (Salipira et al., 2007). The aim of this study was to prepare dual functional polymers to remove organic pollutants from water and destroy bacteria. This was done by impregnating the polymers with the antimicrobial metal, silver.
Functionalisation of multiwalled carbon nanotubes (MWNT)
Multiwalled CNTs (1 g) from SunnanoTM were oxidised using a mixture (40 m.) of nitric acid (HNO3) and sulphuric acid (H2SO4) at a 1:3 ratio for 30 min to incorporate carboxyl (.COOH) and hydroxyl (.OH) groups onto the MWNT. The mixture was then diluted with distilled water and filtered using a PTFE filter membrane (0.47 Êm). The MWNTs were dried in a desiccator at room temperature overnight and characterised using FT-IR spectroscopy.
Synthesis of silver nanoparticles on functionalised MWNTs
Aqueous solutions containing AgNO3, (0.01M) polyvinylpyrrolidone (PVP) (20mM) and ethanol were stirred at 50°C for 2 h (Dai et al., 2007). The functionalised MWNTs were immersed in the aqueous solution, after which ascorbic acid (3.5 g) was added to the mixture which was then stirred for a further 2 h (Wang et al., 2006a). The Ag-MWNT composites were then filtered, washed with double-distilled water (1 .) and dried in an oven at 150oC for 3 h. Characterisation of the silver nanotubes was done using IR spectroscopy to test for the presence of the .COOH and .OH groups required for polymerisation. Transmission electron microscopy (TEM) was used to confirm whether the silver nanoparticles had been loaded onto the functionalised MWNTs.
Polymerisation of silver MWNTs onto cyclodextrin polymers
Ag-MWNTs (0.04 g) were sonicated in dimethyl formamide (DMF) (2 m.) for 15 min. À-cyclodextrin (CD) (4 g) was dissolved in DMF (40 m.) in a round-bottom flask. The Ag-MWNTs (0.04 g) in DMF were then added and the mixture was stirred at 70°C. Hexamethylene diisocyanate (HMDI) (4 m.) was added drop-wise and the reaction was stirred for 24 h under inert conditions. The progress of the reaction was monitored using IR to check for the disappearance of the isocyanate (NCO) peak at 2 700 cm-1. The absence of the NCO peak at the end of the reaction was an indication of the completion of the reaction. The polymer (Ag-MWNT-CD) was precipitated using acetone and dried under vacuum. A grey powdery product was obtained (Salipira et al., 2007).
Other polymers containing no-silver but only the MWNTs (1% MWNT-CD), and a polyurethane containing only the CD (CD(HMDI)), were also synthesised by the same procedure in order to compare the efficacy of all the polymers.
1% MWNT-CD (0.03 g) and Ag-MWNT-CD (0.03 g), and CD(HMDI) (0.03 g) polymers were packed in empty Solid- Phase-Extraction (SPE) cartridges. The cartridges were sterilised by autoclaving. E. coli (ATCC 25925) cells were grown in nutrient broth (Merck) for 24 h and incubated at 37°C while shaking. The E. coli cells were washed several times using phosphate-buffered solution (PBS) and were re-suspended in 10 m. of 0.01 M tetrasodium pyrophosphate. The 10 m. of cells suspended in 10 m. tetrasodium pyrophosphate was then added to 990 m. of sterile distilled water and mixed well. The concentration of E. coli-spiked water was established by serially diluting the water then culturing on nutrient agar plates for 24 h at 37°C. The spiked water was passed through the cartridges packed with the polymers. The cartridges were connected to a separating funnel, which carried the spiked water, and a collection flask. Flow rate was adjusted to 5 m./15 min for 90 min. Funnels had been sterilised by soaking in 5% bleach solution and rinsed using sodium thiosulphate, while the flasks were sterilised by autoclaving.
Water samples were cultured on Chromocult media (Merck) using spread plate and membrane filter methods. Serial dilutions where necessary were done using sterile saline solution. E. coli grows on Chromocult media to form violet colonies. The bacterial cell count was done using the colony count method. The efficiency of the polymers in destroying bacteria was evaluated by comparing the initial and final bacterial count after passing the spiked water through polymer-packed cartridges.
Removal of para-nitrophenol (PNP)
The polymers were further tested for their ability to remove a model organic pollutant in spiked water with a concentration of 10 Êg/g. The polymers (0.03 g) were packed in separate SPE cartridges and 30 m. of the spiked water was passed through the polymer. The resultant filtrate was analysed using ultraviolet (UV) spectroscopy. The PNP absorption maximum is at 318 nm hence all absorbance readings were read at 318 nm.
Nanoparticle leaching studies
Silver-impregnated carbon nanotubes and cyclodextrin polymers were packed in SPE cartridges and were connected to the disinfection set-up. Distilled water (100 m.) was passed through the polymers at flow rates of 5, 30 and 85 m./min. The eluted water was then analysed for the presence of leachedout silver using atomic absorption spectroscopy (Ibarra et al., 2007).
Results and discussion
Functionalisation of MWNT
Oxidation of the multiwalled carbon nanotubes was successfully accomplished, forming functionalised-MWNT (f-MWNTs), as confirmed by IR spectroscopy. The presence of groups such as the carbonyl peak at 1 730 cm-1 and the hydroxyl peak at 3 437 cm-1 confirms the functionalisation of the MWNT. In addition, the f-MWNTs were also soluble in water, while as-synthesised MWNTs are not. This can be attributed to the presence of the -COOH and -OH groups on the surfaces of the f-MWNTs. The oxygen-containing groups also provide active sites that improve the reactivity the MWNTs. These sites also make it possible to load silver nanoparticles on the surfaces of the MWNTs.
Silver nanoparticle impregnation
The synthesis of silver and copper nanoparticles using ascorbic acid as a reducing agent in the presence of polyvinylpyrrolidone, as surfactant, and silver nitrate solution at 0.01M yielded particles that are nano-sized according to the transmission electron microscopy image (Fig. 1) This figure shows the loading of the nanoparticles onto the f-MWNT with a diameter range of 10 to 30 nm. A weak reducing agent like ascorbic acid yields particles ranging from 1 to 10 nm when synthesised in PVP (Wang et al., 2006b). From the TEM image, the presence of dark spots on the outer wall of the carbon nanotubes suggests successful impregnation of silver nanoparticles into f-MWNTs, and was confirmed by EDS analysis.
Synthesis of silver MWNT-CD polymer
The synthesis of the Ag-MWNT-CD polymers was successful. The disappearance of the NCO peak in the IR spectrum marked the completion of the reaction. The polymers were characterised using scanning electron microscopy (SEM) (Fig. 2) and other techniques to determine the surface properties of the polymers. The polymers were found to have a spongy appearance.
Monitoring of water quality for microbial parameters requires the selection and use of indicator organisms. The coliform groups, total and faecal coliforms, are most widely used as indicator organisms, particularly of faecal contamination of water. Escherichia. coli, which is classified under faecal coliforms, has been used worldwide as a specific indicator of bacterial contamination in drinking water. It has also been used for similar research projects to this one (Momba et al., 2003).
The initial count of the spiked water used was found to be 1.3.107 cfu/ml. Table 1 shows the resultant counts after passing the spiked water through the polymers.
From the results shown in Table 1, two trends can be noted. One is that the amount of bacteria which is destroyed by the Ag-CNT-CD polymer increases with time. The second trend is the decrease in the removal of bacteria with time. The Ag MWNT CD showed an initial removal of 94% within the first 30 min of the testing period. After 90 min a 100% removal of bacteria by the silver polymers was observed. No amount of washing of the polymer was able to 'dislodge' viable bacteria from the polymer. With increased contact time the silver-impregnated polymers had an improved antibacterial characteristic. With regards to the polymers that did not contain silver nanoparticles, there was a sharp fall in the removal of bacteria over time. The removal by MWNT CD polymer shows a drop from 84% to 48%, whilst bacteria removal by cyclodextrin(HMDI) polymers decreases from 71% to 48%. The limited removal of bacteria by the metal-free polymers can be attributed to the bacteriostatic properties of carbon surfaces (Park and Jang, 2003). Activated carbon, for example, exhibits a limited bacteriostatic property (Oya and Yoshida, 1995). However, the mode of the bacteriacarbon surface interaction is not known. The phenomenon of antibacterial properties of the silver can be explained by the fact that the metal nanoparticles carry a positive charge which is opposite to the negative charge on the gram negative cell wall of E. coli, thus producing structural changes on the bacterial cell membranes (Zhang et al., 2004).
Removal of para-nitrophenol
The removal of PNP by the silver-loaded polymers was quite low when compared with that of the carbon nanotube and cyclodextrin polymers, and that of native cyclodextrin polymers. Also it is apparent from BET analysis that the silverimpregnated polymers had a low surface area when compared with the silver-free polymers. Silver impregnation of the polymers has a negative effect on the surface area of the polymers. Silver loading also compromises the polymer's ability to remove organics from water.
Silver leaching-out studies
Some concerns have been raised regarding the toxicity of engineered nanomaterials towards the environment and humans. In this study, it was necessary to assess the leachability of silver nanoparticles into the water treated with the silver polymers. Treated water was found to contain less than 0.1 mg/. of silver; silver levels in treated water were below the instrument's detection limit. According to the World Health Organisation's Water Quality Guidelines for Drinking Water, silver levels of 0.1 mg/. could be tolerated without any health risk. This concentration gives a total dose over 70 years of half the human NOAEL (no observed adverse effect level) of 10 g (WHO, 2006). Hence possible leaching of silver into the water when using silverimpregnated polymers does not pose any significant health risk since levels are below 0.1 mg/..
The synthesis of silver impregnated polymers was achieved and was confirmed using various characterisation techniques. The silver-loaded polymers displayed an improved ability to destroy bacteria in water when compared to the native carbon nanotube and cyclodextrin polymer and the cyclodextrin polymer. From the results, it can be concluded that metal loading does improve the antibacterial properties of the polymers and can be used as an alternative disinfection material.
In the removal of organics from water, the metal-loaded polymers do not perform as well as the native carbon nanotubes and cyclodextrin polymers. It appears that there is a relation between the adsorption of organics and the surface area of the polymers but no concrete conclusions can be drawn at this stage.
Funding from National Research Foundation, Nanotechnology Innovation Centre, Centre of Excellence in Strong Materials and the University of Johannesburg is gratefully acknowledged.
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LP Lukhele1, RWM Krause1*, BB Mamba1 and MNB Momba2
1 Department of Chemical Technology, University of Johannesburg, PO Box 17011, Doornfontein 2028, South Africa
2 The Department of Environmental, Water and Earth Sciences, Tshwane University of Technology, Arcadia Campus, Private Bag X680, Pretoria 0001, South Africa
* To whom all correspondence should be addressed.
* +27(11) 559 6152; fax: +27(11) 559 6425; e-mail: email@example.com
Received 4 February 2010; accepted in revised form 31 May 2010.