Scientific Data

Scientific Data

Antibacterial Properties and Mechanism of Activity of a new Silver-Stabilized Hydrogen Peroxide (Boosted Disinfection)

Trade Marks: HSP (USA) & GBM (Europe)

Nancy L. Martin, 1 ,* Paul Bass, 2 and Steven N. Liss 2 , 3 ,*

Andrew C Singer, Editor

Author information, Article notes, Copyright and License information, Disclaimer

Aim of this study

The aim of this study was to evaluate HSP (USA) branded GBM (Europe) against both Gram negative and positive bacteria and to examine the HSP mechanism. This study compares the disinfection efficacy of HSP, lab grade H2O2, and NaOCl minimum inhibitory concentrations for suspended (planktonic) cultures of indicator bacteria. The activity of HSP, H2O2, and the proprietary silver solution present in HSP/GBM were examined separately to evaluate the contribution of each component to bacterial killing. The results demonstrate that HSP/GBM, preferentially interacts with the bacterial cell surface in a manner likely mediated by silver, thereby concentrating the biocidal activity of HSP/GBM of its target virus, significantly boosting efficacy.

Associated Data

Data Availability Statement


Chlorine or sodium hypochlorite (NaOCl) has long been used as an effective disinfectant for drinking water [1], its use first coming into practice during the mid 1880s to help deal with typhoid fever epidemics in the port of Pola on the Adriatic Sea and in Maidstone, England [2]. Since that time, owing to the important public health outcome from the inactivation of microbial pathogens, the demands for cost effective, large-scale provision of potable water have driven an expansion in the use of chlorination worldwide. Communities ranging in size from large urban centres to individual family homes in rural settings all require access to safe drinking water that is provided through a wide variety of distribution system types. These systems experience a range of operational issues that are often of a microbial character, such as persistence of pathogens and development of microbial biofilms for which disinfection or microbial control strategies are important [3].

In addition to drinking water, chlorination is frequently used for disinfection of water in swimming pools [4] and tertiary treatment of wastewater [1]. Increasingly however, evidence suggests that the residual byproducts of water disinfection when using chlorination, such as trihalomethanes, can have negative health effects [5–7]. In addition, environmental conditions can occur where chlorine is not effective in adequately disinfecting water, leading to risk of infection [2, 8, 9]. Alternative measures to chlorination or post-chlorination applications that mitigate the negative aspects could extend the usefulness of chlorine in providing safe drinking water.

Hydrogen peroxide (H2O2) has also been used for many years for water disinfection [2] and is generally considered to have low ecotoxicity as well as having no odor or colour [10, 11]. Oxidizing agents such as H2O2, also commonly known as reactive oxygen species (ROS), have also been extensively used as antiseptics however, until recently, their lack of specificity to microbial cells over host/mammalian cells have tended to limit the use of H2O2 to topical therapeutic applications [12]. In order for H2O2 to be an effective microbicide it must be able to overcome the myriad of cellular mechanisms that are in place to deal with ROS that occur normally due to aerobic respiration, as well as inducible defence mechanisms that provide antioxidizing activities in the presence of exogenous oxidants, a situation termed oxidative stress. Bacterial pathogens have probably evolved ROS-responsive defence mechanisms to help deal with oxidative killing that is part of the host defence against invading microbes [12]. One common bacterial strategy to deal with excess H2O2 is to degrade H2O2 via enzymes collectively termed catalases; monofunctional catalases catalyze the disproportionation reaction while bi-functional catalases have both H2O2 degrading and H2O2 reducing activities [13]. In addition, organisms frequently contaminating water such as E. coli, produce several peroxidases such as NADH peroxidases, thiol peroxidase, cytochrome C peroxidase, bacterioferritin comigratory protein, glutathione peroxidase, and rubrerythrins, all to deal with H2O2 [13]. As little as 1 μM H2O2 can oxidize the cellular pool of free ferrous iron, thereby generating hydroxyl radicals that can cause significant DNA damage [14] via the Fenton reaction [15], therefore the pool of H2O2 scavenging enzymes is diverse.

Dental unit water systems, used to irrigate patients’ mouths during treatments, pose a significant water disinfection challenge as they are often contaminated with high numbers of bacteria, including opportunistic pathogens and organisms frequently forming biofilms. A recent study looked at combinations of silver and H2O2, as well as other compounds, to disinfect the dental units and found a silver/ H2O2 combination to be the most effective [16]. Early studies examining the biocidal effects of hydrogen peroxide combined with ionic silver clearly showed a synergistic killing effect against Escherichia coli [17, 18] while more recent studies have examined efficacy against a broader range of Enteriobacteriaceae [19] and organisms commonly found in swimming pools [20] while more recently silver is employed in nanoparticle formulations [21].

Silver, a biologically non-essential metal, has been investigated and used as a biocide for many years [22], where multiple strategies are being proposed for treatment of drinking water [23–25]. Treatment of drinking water systems with silver in combination with copper [26, 27] and of hospital hot water systems with a silver/hydrogen peroxide compound [28] to prevent Legionella has been shown to be efficacious. The World Health Organization deemed that up to 100 ug/L (ppb) silver could be present in drinking water without posing health risks [29]. The monovalent silver cation (Ag[I]) is the active species, interacting with amines, hydroxyls, phosphates and thiols via their nitrogen, oxygen and sulfur-containing electron donating groups both at bacterial membranes and within the cell [21, 22]. These interactions ultimately lead to disruption of the proton motive force, deregulation of the electron transport system and increased membrane permeability leading to cell death [21].

HSP (USA) or GBM (UK), a recently developed H2O2 that is stabilized with the addition of low concentrations of ionic silver (0.013–0.017%), is designed for application in the disinfection of water and medical and veterinary-related uses and Volume area disinfection through fogging [30]. The first North American site to employ hydrogen peroxide in drinking water (Killaloe Water Treatment Plant has been part of recent pilot studies approved by the Ontario Ministry of the Environment, and under the auspices of the Ontario Clean Water Agency, investigating the application of HSP as a secondary disinfectant. Unpublished data indicates that HSP can be successfully used as a secondary disinfectant, contribute to the significant reduction of trihalomethanes, and that residual levels of HSP remained throughout the distribution system. Although synergistic antimicrobial properties provided by a combination of H2O2 and ionic silver were previously demonstrated using silver nitrate to which H2O2 had been added [17–20], there are no published studies examining the biocidal properties or mechanism of HSP. While the biocidal mechanisms of H2O2 [31]or silver [21] are well studied, the synergistic mechanism of combined formulations of silver and H2O2 are poorly understood.

The aim of this study was to evaluate HSP against both Gram negative and positive bacteria and to examine the HSP mechanism. This study compares the disinfection efficacy of HSP, lab grade H2O2, and NaOCl minimum inhibitory concentrations for suspended (planktonic) cultures of indicator bacteria. The activity of HSP, H2O2, and the proprietary silver solution present in HSP were examined separately to evaluate the contribution of each component to bacterial killing. The results demonstrate that HSP, but not H2O2, preferentially interacts with the bacterial cell surface in a manner likely mediated by silver, thereby concentrating the biocidal activity of HSP of its target virus, significantly boosting efficacy.

Materials and Methods

Strain and culture conditions

Laboratory strains of E. coli K12, P. aeruginosa PAO1, B. subtilis and S. aureus were acquired from Queen’s University’s microbiology unit strain collection. Environmental E. coli strains were collected in Kingston, Ontario by Dr. Aston of Queen’s University and were as follows: Lake Ontario water sample 1 (LOWS1), Lake Ontario water sample B6 (LOWS1-B6), Commodore’s Cove Lake 1 (CCL1), and Cataraqui Mall pond (CMP-B11A). The E. coli K12, B. subtilis, and environmental E. coli isolates were maintained on Luria Bertani (LB) agar while the S. aureus and P. aeruginosa PAO1 isolates were maintained on full strength Tryptic Soy agar (TSA). For starting inocula a single colony was picked from the respective agar plate, transferred to 50 mL of the appropriate growth medium and incubated for 17 hours with aeration (150 RPM shaking) at 37°C.

Media and solution preparation


Luria Bertani (LB) broth was prepared by dissolving 10 g of tryptone, 5 g of yeast extract and 5 g of sodium chloride (Fisher Scientific, Ottawa, ON, Canada) in a final volume of 1 L Millipore MilliQ (Millipore Canada, Toronto, ON, Canada) distilled and deionized water (MDD). Full strength tryptic soy broth (TSB) was prepared by dissolving 30 g of Bacto TSB Soybean-Casein Digest powder (BD Biosciences, Mississauga, ON, Canada) in a final volume of 1 L with MDD. The tap water used in this study was de-chlorinated by vigorously stirring 1 L volumes with a stir bar for a minimum of 16 hours. After de-chlorination, the tap water was adjusted to either pH 7.0 or 8.5 and filter sterilized using a 0.22 μm filter. The saline (0.9% NaCl), CaCl2 and KCl solutions (Fisher Scientific, Ottawa, ON, Canada) were all prepared as 1 M stock solutions and diluted to the appropriate working concentrations using MDD. Tris buffer (10 mM; Fisher Scientific, Ottawa, ON, Canada) was used to buffer the CaCl2 and KCl solutions at pH 7 and the tap water at pH 7.0 and 8.5. For the synthetic MIC, CT and cell-associated assay starting inoculums, a synthetic wastewater media [32] was prepared daily with a chemical oxygen demand (COD) of approximately 600 mg/L and a COD: Nitrogen: Phosphorus ratio of 100:5:1 [final concentrations of 250 mg/L glucose and 283.5 mg/L sodium acetate for the carbon sources, 8.78 mg/L KH2PO4, 11.24 mg/L K2HPO4 for the phosphorus source, 89.33 mg/L of (NH4)2SO4 for the nitrogen source, 5.07 mg/L MgSO47H2O, 2.0 mg/L CaCl22H2O, 0.01 mg/L NaMoO42H2O, 0.36 mg/L MnCl24H2O, 0.50 mg/L FeSO47H2O, 0.39 mg/L CuSO45H2O, 0.44 mg/L ZnSO47H2O and 0.41mg/L Cl26H2O for the trace metal sources,3.0 mg/L Fe(III) EDTA for the iron source and 100mg/L yeast extract]. The Fe (III) EDTA solution was prepared as per EDTA [33]. Agar plates were prepared by adding 15 g of granulated agar (Fisher Scientific, Ottawa, ON, Canada) to 1 L of the respective media.

Test products

Three oxidizing biocides were selected: laboratory grade 3% Hydrogen Peroxide (Fisher Scientific, Ottawa, ON, Canada), laboratory grade 5% Sodium Hypochlorite (RICCA Chemical Company, Arlington, TX, USA) and 19.9% HSP (SanEcoTec Ltd, Ottawa, ON, Canada). Two types of silver were tested. First, was the proprietary silver solution found in HSP, termed “H-Silver” (SanEcoTec Ltd, Ottawa, ON, Canada), which was received as a concentrated stock solution containing 363 ppm silver (concentration confirmed by Flame Atomic Absorption Spectroscopy (Agilent Fast Sequencer (FS) 280), Queen’s University Analytical Services). The second was certified ACS silver nitrate (Fisher Scientific, Ottawa, ON, Canada). All working solutions were prepared aseptically with sterile media immediately before conducting the experiments.

Neutralizer preparation

The catalase: peroxide ratio for successful neutralization of peroxide was determined to be at least 1:2. A stock solution of 3.4% bovine liver catalase (Sigma-Aldrich, St. Louis, MO, USA) was diluted to the appropriate working concentration aseptically in sterile test media. Sodium thiosulfate (Fisher Scientific, Ottawa, ON, Canada) was used for neutralizing hypochlorite as indicated by [34]. In the current study a 6% solution of sodium thiosulfate was used to ensure neutralization of the chlorine. After employing the neutralizers, chlorine and peroxide test strips were used to measure residual levels of biocide; a reading of 0 ppm indicated sufficient neutralization.

Sterility techniques used for the reagents

Ultrapure water (Millipore MilliQ, Millipore Canada, Toronto, ON, Canada), nutrient rich media, stock synthetic wastewater media components (except for Fe (III) EDTA), saline, KCl and CaCl2 were all sterilized by autoclaving. The Fe (III) EDTA, pH controlled de-chlorinated tap water, sodium thiosulfate and catalase were filter sterilized using a 0.22 μm filter.

Minimum inhibitory concentration (MIC) assays

MIC assays determined the minimum concentration of disinfectant required to inhibit the overnight growth of planktonic bacteria [35]. A variety of different organisms were tested in nutrient rich media (TSB or LB broth) and synthetic wastewater media. The desired test medium was inoculated with a pure culture and incubated for 17 hours with aeration at 37°C. The same type of media was used in flat bottom 96 well microtitre plates (Sarstedt, Saint Léonard, QC, Canada) to determine the MIC. Initially, MIC ranges were determined using 2 fold successive dilutions of biocide to achieve the desired concentration range. Inocula of 106 CFU/mL, standardized using a predetermined conversion factor relating CFU/mL to OD600, were prepared in 10 mL volumes and 50 uL was added resulting in a final inoculum concentration of 5 X 105 CFU/mL. Positive growth controls (50 uL media +50 uL inoculum) and negative growth controls (100 uL media) were included. The microtitre plates were incubated in static conditions overnight at 37°C. Using a Varioskan (Thermo Scientific, Burlington, ON, Canada) spectrophotometer, the optical density (OD600) in each well was measured. An OD600 greater than 0.1 was considered to be positive growth. Once a preliminary MIC range was determined, subsequent MIC assays over narrower concentration ranges were conducted to determine a more accurate MIC.

Contact/kill Time (CT) assays

CT assays determined the bacterial killing achieved after various durations of exposure to 20 ppm of disinfectants. The bacterial loads tested were 106 CFU/mL and 103 CFU/mL E. coli K12 in tap water (pH 7/8.5). Synthetic media was inoculated with 1 mL of pure culture (culture containing 1 genus/species only), and incubated for 17 hours with aeration at 37°C. To rinse the cells, aliquots of a 17 hour culture were spun down at 14,000 x g for 5 minutes and re-suspended in sterile de-chlorinated tap water. The rinsing process was repeated twice before taking the OD600 reading. Using a predetermined conversion factor relating CFU/mL to OD600, 103 or 106 CFU/mL cultures were prepared in 10 mL of sterile, de-chlorinated tap water buffered with 10 mM TRIS at the desired pH. Disinfectants were added to 10 mL cultures at 20 ppm with moderate shaking for the duration of the experiment. At multiple time points, an aliquot was removed and mixed with the neutralizing solution. The neutralized mixtures were serially diluted in de-chlorinated tap water and 100 uL of each dilution was plated on LB agar; the plates were incubated for 17 hours at 37°C. The CFU/mL were calculated by counting plates with between 5–300 colonies from the various time points and multiplying by the required dilution factor.

Neutralization of biocides

Assays were designed to determine if the biocide was being completely neutralized during the CT assays. As per the time-kill assays, 103 and 106 CFU/mL E. coli K12 cultures were prepared in sterile tap water at pH 7 and exposed to 20 ppm HSP or peroxide. At the desired time points, four 500 uL aliquots were removed and spun down at 14, 000 X g for 5 minutes. Following centrifugation, 450 uL of supernatant was removed and discarded. Two of the pellets were re-suspended in 450 uL of sterile, de-chlorinated tap water (pH 7) and the other two pellets were re-suspended in 450 uL of 20 ppm sterile catalase. These were serially diluted in sterile de-chlorinated tap water (pH 7) and 100 uL of each dilution was plated on LB agar. The plates were incubated for 17 hours at 37°C. CFU/mL were calculated by counting plates with between 5–300 colonies from the various time points and multiplying by the required dilution factor.

Determining the effect of KCl and CaCl2 on the killing efficacy

CT assays were performed in KCl and CaCl2 solutions to determine if the presence of mono and divalent ions in solution would influence the killing efficacy of HSP and H2O2. The experiments were conducted exactly as previous CT assays, however in addition to testing in tap water, solutions of 0.005, 0.015, 0.025 and 0.05 M KCl and CaCl2 were used. Tris buffer (10 mM, pH7) was included. After 60 minutes of contact time, catalase neutralizing solution was added, cultures were serially diluted and 100 uL of each dilution was plated on LB agar. The plates were incubated for 17 hours at 37°C. The CFU/mL values were calculated by counting plates with between 5–300 colonies and multiplying by the required dilution factor.

Carbon dioxide measurement

A Continuous Emissions Monitoring System (CEMS) for measuring carbon dioxide was constructed as described by [36]. A silicone tube biofilm reactor (inside diameter, 0.16 cm; outside diameter, 0.24 cm; length, 150 cm; VWR International, Mississauga, ON, Canada) was encased in a sealed Tygon tube (inside diameter, 0.48 cm, outside diameter, 0.79 cm; formulation R-3603; VWR International, Mississauga, ON, Canada). The annular space of the CEMS was connected to an absolute, nondispersive, infrared LI-820 CO2 gas analyzer (LI-COR Biosciences, Lincoln, NE, USA) and CO2 free compressed air (Linde Canada Limited, Kingston, ON, Canada) was used as a sweeper gas. Gas flow rates were controlled by an HiQ Baseline brass 1-stage regulator with an NPT female outlet (Linde Canada Limited, Kingston, ON, Canada) and a thermal gas mass flow meter set to 9.5 mL/min (Aalborg, NY). The Li-820 CO2 gas analyzer was calibrated using a two-step calibration process. First, the analyzer was zeroed by running the CO2 free compressed air through the analyzer and manually setting the CO2 reading to 0 ppm. Subsequently, an 1800 ppm CO2/air mixture (Linde Canada Limited) was passed through the system while the CO2 reading was manually set to 1800 ppm. The 1800 ppm CO2/air calibration gas’s flow rate was controlled using the previously mentioned HiQ Baseline regulator.


After assembly of the CEMS, the apparatus was disinfected with 0.525% NaOCl in dH2O for a minimum of 2 hours. Subsequent overnight irrigation (minimum 16 hours) with dH2O rinsed the bleach from the tubes. Prior to inoculation, sterile 1% TSB was flushed through the tubes for 30 minutes to displace the dH2O. As per a modified version of Kroukamp and Wolfaardt’s [36] procedure, pure culture biofilms of P. aeruginosa PAO1 were grown in the silicone tubes. Using a sterile needle and syringe, the silicone tubes were inoculated with 200 μL from an overnight culture grown in 10% TSB; the pump was turned off for 30 minutes to allow initial adhesion to the tube walls. After adhesion, sterile 1% TSB was continuously supplied by a Masterflex L/S peristaltic pump (Cole Parmer Canada Inc., Montreal, QC, Canada) at 21 mL/min. All biofilms were developed until CO2 levels indicated a steady metabolic state was achieved for 20 hours at 25°C using a water bath to control the temperature.

Biocide treatment of biofilms

After the biofilm reached a steady metabolic state, the inflowing medium was switched to freshly prepared HSP, HSP-Silver or silver nitrate solutions in 1% TSB. The tested HSP concentrations were 70, 100, 140 and 500 ppm, which respectively contained HSP-Silver concentrations of 50, 75, 100 and 375 ppb. Tested molar concentrations of silver from silver nitrate matched the (HSP) or (GBM) concentrations. The duration of each constant flow exposure was 2 hours; post exposure, the inflowing medium was switched back to 1% TSB and the biofilms initiated their recovery process. Throughout the exposure and recovery process, fluctuations in CO2 production rates were monitored. Once the biofilm recovered to a steady metabolic state for 20 hours after the initial exposure a second treatment with the same biocide was carried out. After the second exposure was complete, the CEMS was sterilized and a new biofilm was initiated as described in section 2.11.

Viable cell counts and live/dead cell imaging

Approximately 1.5 mL of effluent was collected from the disconnected downstream tubing at time = 0 hours (once the biofilm achieved a steady metabolic state for 20 hours) and at time = 2 hours (once the 2 hour exposure to the test solution concluded). The effluent was spun down at 14,000 X g for 5 minutes and re-suspended in sterile 0.9% NaCl twice. The effluent was serially diluted in sterile 0.9% NaCl and plated on 10% TSA. After 24 hr incubation at 37°C CFU/mL values were calculated by counting plates with between 5–300 colonies and multiplying by the required dilution factor.

A modified version of a viable cell count procedure [36] was carried out and additional effluent was collected and washed for epifluorescent microscopic imaging. Using a live/dead BacLight Bacterial Viability Kit (Invitrogen Canada, Burlington, ON, Canada), bacterial viability was determined as per the manufacturer’s protocol. Prepared slides were examined with 40 X magnification at the objective using a confocal microscope (Zeiss LSM710, Carl Zeiss Canada, Toronto, ON, Canada) equipped with an Argon 488 laser. The number of live and dead cells per microscope field was analyzed using the image analysis software provided by the manufacturer and live:dead ratios were calculated.


Minimum Inhibitory Concentrations (MICs) of biocides

A panel of Gram negative or positive laboratory and environmental isolates was selected to compare the MICs for HSP, H2O2, and NaOCl. These results are not meant to indicate absolute MIC values for each biocide/organism, but rather are a means to compare biocide susceptibility under a defined set of conditions as it is well established that MICs can vary significantly depending upon inoculum size, media, and the length of incubation [37]. Table 1 summarizes data comparing MICs in either rich media (tryptic soy broth or Luria broth) or synthetic wastewater media (SYN) for selected test organisms. Bacteria showed greater susceptibility to all biocides in SYN versus rich media. Environmental isolates of E. coli were slightly more susceptible to HSP or H2O2 than the K-12 laboratory strain, however some environmental isolates had a higher NaOCl MIC than the K-12 strain. When comparing the susceptibility to HSP and H2O2 MICs were very similar, with B. subtilis being the most sensitive, followed by P. aeruginosa, E. coli and then B. subtilus over a range of 8 to 59 ppm biocide in rich medium. Of these 4 strains P. aeruginosa was the most resistant to NaOCl.

Table 1

Minimum inhibitory concentration (MIC) range of biocides for microorganisms tested in nutrient rich and synthetic wastewater media (105 CFU/mL inoculum).

Bacteria Media 1 HSP H2O2 NaOCl
P. aeruginosa PAO1 TSB 24–40 32–40 640
B. subtilis SYN 10 15 80
B. subtilis LB 59 59 400
B. subtilis SYN 25 25 30–70
S. aureus LB 8 8 309–463
S. aureus SYN 10-25 10 50-90
E. coli K12 LB 39–49 39–59 294–412
E. coli K12 SYN 10–15 10–15 10–30
E. coli CMP-B11A LB 24–30 24–30 350
E. coli CCL1 LB 32 24–32 300–400
E. coli LOWS1 LB 32–40 32–40 350–400
E. coli LOWS1-B6 LB 25–40 30–40 294–412
E. coli KS1 LB 30–36 42 480
E. coli KS2 LB 36 36 320

1TSB—Tryptic soy broth; LB- Luria Bertani; SYN—synthetic wastewater media

Killing efficacy of biocides is pH and bacterial cell density dependent

In order to determine the ability of the biocides to kill the test bacteria in a time dependent manner E. coli were treated with the same concentration (20 ppm active) of each biocide and, at multiple time points, the number of viable cells was determined after neutralization of the biocide (Fig 1). To determine the effect of pH on killing efficacy, killing time at pH 7.0 versus 8.5 was examined (Fig 1A and 1B). At pH 7.0 all bacteria were killed with either HSP or NaOCl within 120 minutes, whereas exposure to H2O2 resulted in a 1–2 log reduction in 300 minutes. At pH 8.5, killing efficacy by H2O2 was reduced to slightly over 300 minutes of exposure, while the time for complete killing by NaOCl increased to 180–240 minutes and HSP increased slightly to 120–180 minutes.

Fig 1.

Fig 1
Comparison of pH and cell density dependent killing efficacy of HSP, H2O2, and NaOCl Killing efficacy of biocides (20 ppm) at pH 7.0 on 106 E. coli (A), at pH 8.5 on 106 E.coli (B), and at pH 7.0 on 103 E. coli (C) as measured by total CFU/mL over 300 min (A,B) or 60 min (C).
H2O2 is much slower at killing bacteria at pH 7.0 than either HSP or HOCl2 (A). Raising the pH to 8.5 increases the 100% kill times of NaOCl to equal to or greater than that of HSP (B). At lower cell densities HOCl2 reaches 100% killing in 15–30 minutes while both HSP and H2O2 show even faster killing kinetics (C).

The effect of bacterial density was tested by comparing the killing efficiency of 106 cells/mL with 103 cells/mL. Killing of 103 bacteria with NaOCl reached 100% by 15–30 minutes, a slightly higher efficiency than with 106 cells. H2O2 killing efficiency was the same with 103 and 106 bacteria within 60 minutes. Unpredictably, at 60 minutes less than 1 log reduction was achieved with HSP using 103 bacteria compared with approximately a 3 log order reduction of culturable cells when starting with 106 bacteria. Contrary to expectations, based on the ratio of bacteria to biocide molecules where it was anticipated that fewer bacteria would be killed faster under the same parameters, HSP performed differently. After removing bacteria from the HSP solution by centrifugation, HSP killing kinetics were inverse to expectations, with higher bacterial concentrations being killed more efficiently. This result prompted an examination of the effect of neutralization of the biocide on kill times at the two bacterial concentrations with HSP versus H2O2.

Differences in susceptibility of HSP and H2O2 to neutralization by catalase

Neutralization of the biocides was being carried out in order to quickly stop the killing effect of the biocides while the bacteria were being prepared for plating by pelleting the bacteria, discarding the biocide-containing supernatant and diluting the bacteria for determination of CFU. Preliminary experiments had shown that to halt killing it was insufficient to remove bacteria from the biocide solution, especially when testing HSP (data not shown). Any biocide associated with the bacterial cell would remain with the cell after centrifugation. When the killing rate of 106 bacterial cells was examined with or without neutralization there was no difference with either HSP or H2O2 although HSP was more effective at killing than H2O2 as previously shown (Fig 2A and 2C). There was little killing by H2O2 using 103 bacterial cells and no difference in the presence or absence of neutralization (Fig 2D). When 103 cells were tested with HSP, there was a significant difference in killing rate in the presence and absence of neutralization, with the bacteria being killed much more quickly in the absence of neutralization (Fig 2B). This result suggested that HSP was interacting with bacterial cells differently than H2O2. The data suggested that at bacteria (cells): HSP(ppm) ratios of 106:20 most of the HSP was bound to the bacterial cell surface and neutralization was inefficient. Thus, when the bacterial concentrations were lower, neutralization was likely more efficient owing to the higher levels of disinfectant in solution. This is further supported by the observation that, in the absence of neutralization, significant levels of active biocide remained associated with the bacterial cells after centrifugation (Fig 2B). H2O2 however, did not show the same killing kinetics (Fig 2D). When the bacteria were separated from the soluble H2O2 via centrifugation, killing almost completely ceased suggesting that once the soluble H2O2 is removed or neutralized, there is little to no cell associated effect.

Fig 2.

Fig 2
Comparison of the effect of neutralization of biocide on killing of E.coli at high and low cell densities.
Killing efficacies of HSP or H2O2 (20 ppm) was measured at high (A, C) or low (B, D) cell densities with and without neutralization of biocide by addition of 20 ppm catalase. Killing rates at high cell densities by HSP or H2O2 are not influenced by neutralization (A, C), whereas at low cell densities bacteria exposed to HSP, but not neutralized, are killed significantly more quickly than those neutralized (B). This effect is not seen with H2O2 at the low cell densities (D).

Effect of mono and divalent cations on biocide killing efficacy

The initial interaction of HSP with the bacterial cell surface could be of an electrostatic nature due to the presence of positively-charged silver ions. It was predicted that the addition of mono or divalent cations to the biocide solution would compete with HSP, but not H2O2, and alter the killing efficacy. It was demonstrated that KCl and CaCl2 solutions from 0.005 to 0.05 M showed a significant ability to inhibit killing of E. coli by HSP while these salts had no effect on H2O2-mediated killing. In addition, the magnitude of inhibition by the divalent CaCl2 was greater than that of monovalent KCl (Table 2). These data support bacterial cell surface interactions as an important step in the mechanism of HSP killing that is not seen with H2O2 and therefore attributable to the silver present in HSP.

Table 2

Effect of mono and divalent salt concentrations on the killing efficacy of 20 ppm HSP or H2O2 against 106 CFU/mL E. coli K12 at pH 7.

Percent killing

Salt concentration (M)

Salt 0 0.005 0.015 0.025 0.05
HSP KCl 100 85 76 70 84
HSP CaCl2 100 58 60 43 45
H2O2 KCl 100 100 94 91 100
H2O2 CaCl2 100 100 100 100 100
No Biocide KCl 0 1 0 3 3
No Biocide CaCl2 0 3 5 1 2

All values are normalized to killing in the absence of cations.

Comparison of silver-mediated antimicrobial activity on biofilms

To distinguish the effect of silver and H2O2 on the metabolic activity of a P. aeruginosa PAO1 biofilm, a comparison of the antimicrobial activity of HSP was carried out with either silver formulated in the same manner as in HSP but not associated with H2O2 (HSP-Silver), as well as silver supplied in the form of silver nitrate. After establishment of a stable biofilm within a continuous flow cell, it was treated with several concentrations of HSP and corresponding concentrations of ionic silver over the range of 70–500 ppm and 50–375 ppb, respectively, and the reduction in metabolic activity, measured by CO2 levels, was monitored (Fig 3A). Increasing concentrations of HSP showed a dose dependent effect reaching an 83% reduction in CO2 emission at the highest concentration used (500 ppm). HSP-Silver or silver nitrate were found to have no, or a negligible, effect on metabolic activity over two hours of continuous exposure (Fig 3A).

Fig 3.

Fig 3
Comparison of HSP, HSP-silver and silver nitrate on the metabolism and cell viability of a P. aeruginosa biofilm in a continuous flow apparatus.
Stable, established biofilms of P. aeruginosa monocultures were exposed to the indicated concentrations of HSP, HSP-silver or silver nitrate for 2 hrs and CO2 generated was monitored and plotted as the maximum reduction relative to the untreated biofilm pre biocide exposure (A). While silver nitrate and HSP-silver had negligible effects on metabolism, HSP treatment of the biofilm significantly inhibited metabolism. (B) and (C) show the viability of planktonic cells released from the biofilm measure by total viable count (B) or by enumerating live and dead bacteria via epifluorescence microscopy using the BacLight Bacterial Viability Kit (C). Treatment with HSP shows a dose dependent effect on cell viability at more significant levels than either HSP-silver or silver nitrate. Stars indicate HSP treatments statistically significantly different from silver treatments (P ≤0.05) Bars are included where HSP treatment is significantly different from only one type of silver treatment.

Additional measures of biocide/silver activity were obtained by quantifying the number of viable cells (Fig 3B) and by calculating the ratio of live to dead bacteria released into the bulk liquid from the CEMS effluent (Fig 3C). After exposure to the previously described concentration range, HSP reduced the number of viable cells by 37% to 99% with increasing concentrations of biocide compared to 12% (100 ppb) or 15% (375 ppb) for silver nitrate and 33% (75 ppb), 37% (100 ppb) or 97% (375 ppb) for HSP-Silver. Furthermore, direct fluorescent microscopic counts showed a HSP concentration dependent decrease similar to the results from recovering culturable bacteria to a low of a 1:1 live:dead cell ratio at the highest biocide concentration. Live:dead ratios of cultures treated with either silver nitrate or HSP-Silvermaintained much higher viability levels, although HSP-Silver treated cultures had a live:dead ratio of only 2 at the highest silver concentration.


The three biocides that were chosen for comparison in this study are commonly used for water disinfection and spray delivery where they affect microbial viability via the production of reactive oxygen species (ROS) that cause damage to enzymes and DNA within the bacteria cell [38]. Since ROS, such as superoxide (O- 2), H2O2, and hydroxyl radicals (HO) are constantly generated as a result of the normal metabolism of oxygen, both prokaryotic and eukaryotic organisms have evolved a complex array of mechanisms to sequester and inactivate low levels of ROS [38, 39]. Biocide concentrations must therefore be maintained at levels higher than can be accommodated by the target organisms in order to be effective. Biocide concentrations applied must also take into account the impact of various environmental conditions that may compromise the efficacy of the biocide.

The most active aqueous species formed by dissolution of NaOCl in water, hypochlorous acid (HOCl), is predicted to cause irreversible unfolding and aggregation of bacterial cellular proteins, especially thermolabile proteins, which ultimately leads to cell death [40]. NaOCl has been shown to be more potent than most other known oxidants but this potency is highly affected by environmental conditions such as pH and the presence of inorganic and organic molecules [41]. This effect was demonstrated in both the MIC determinations (Table 1) and the kill time tests (Fig 1) using NaOCl. Synthetic wastewater media, which contains a much lower level of organics than Luria Bertani or tryptic soy broth, promoted a much higher efficacy of NaOCl killing than rich media with all bacteria tested. A higher bacterial load, which can be considered a higher organic load, also increased the killing time of NaOCl when killing of 106 CFU/mL was compared to killing of 103 CFU/mL (Fig 1C) of E. coli. At a pH of 7.0 to 8.0, hypochlorous acid dissociates into the much less effective hypochlorite ion (OCl-), thereby decreasing the killing efficacy [41]. The kill time tests carried out at pH 7.0 and pH 8.5 (Fig 1A and 1B) showed increased kill times of E. coli with NaOCl at the higher pH, reflecting a predicted loss in biocidal activity at the higher pH. When comparing the NaOCl susceptibility of the various organisms tested, P. aeruginosa required the highest NaOCl concentrations, B. subtilis and S. aureus fell in the middle with E. coli requiring the lowest, although some environment E. coli strains showed lower susceptibility to NaOCl mediated killing. This general pattern of bacterial sensitivity to NaOCl follows that demonstrated previously [42].

While still a highly effective disinfectant of surfaces, chlorination of drinking water and the subsequent generation of residuals, such as trihalomethanes among a long list of disinfectant by-products [5], have become a significant concern due to their toxicity and mutagenicity [4–7, 43, 44]. New approaches to water disinfection are called for. In addition to being a biocide, peroxide, via the combination of H2O2 and Fe2+ known as the Fenton reaction [15], can also be used to reduce the levels of some of the problematic by-products of chlorine treatment of water [45, 46]. As a biocide H2O2 can oxidize, via the Fenton reaction, iron-sulphur clusters in a number of bacterial dehydratases, thereby inactivating them causing cell death [38]. H2O2 is relatively small and uncharged and is thought to cross membranes as efficiently as water. Endogenous concentrations of H2O2 are low, such that at extracellular H2O2 concentrations of 0.2 μM or greater, H2O2 will tend to move into the cell [47]. While the concentration of 20 ppm (~600 μM) H2O2 used in the current study would therefore be toxic to bacteria, most organisms have developed a complex array of oxidative stress responses that result in the upregulation of ROS scavenger molecules such as peroxidases and catalases that degrade H2O2 in an attempt to protect the cell [38].

A comparison of the MICs determined for both H2O2 and HSP show them to be very similar for all the bacteria tested (Table 1). These MICs are not identical from species to species however, which at least in part, reflects the ability of a particular bacterium to produce catalase. P. aeruginosa [48–50], B. subtilis [51], and E. coli [13, 52, 53], produce multiple catalases and hydroperoxide reductases, while S. aureus produces one of each [54]. For example, E. coli is proposed to synthesize at least nine enzymes that act as catalases or peroxidases [13]. This may account for the greater sensitivity to HSP and H2O2 of S. aureus compared to other tested bacteria. The wide variety of experimental methods commonly used to compare sensitivity to biocides makes comparison with previous results difficult however trends were similar [18–20] to those reported here. There also appears to be a difference in sensitivity to HSP and H2O2 between the MIC values and contact/kill time testing that used 20 ppm biocide (Table 1, Fig 1). Since the MIC testing was an endpoint determination with a 16 hr incubation time in the presence of biocide, it is likely that a small number of bacteria survived higher biocide levels by mounting a protective oxidative stress response upon initial exposure to biocide and then as the biocide levels decreased due to inactivation by catalase production over 16 hrs, bacteria were able to collectively recover similar to experiments reported by Davoudi et al.[19].

It was also determined that HSP suppressed activity against bacteria growing in a biofilm for up to 27 days after initial contact. Bacterial biofilms are an important target of biocides used for water purification as biofilms represent an often difficult to treat mode of bacterial growth [9]. P. aeruginosa biofilms established within a continuous flow cell model system [36, 55, 56] were used here to test biocide efficacy by monitoring metabolic activity while being exposed to varying concentrations of HSP and silver. HSP, the form of silver present in HSP (HSP-silver), and silver from silver nitrate, were compared at equal silver concentrations. The metabolic activity of the biofilm, as measured by CO2 generation, clearly showed a significant inhibition by HSP, albeit at higher concentrations than previously seen to be effective for planktonic cells (Fig 3A). Concentrations of 70–140 ppm HSP decreased cell viability by 33–37% (Fig 3B) or resulted in live:dead ratios of 3.6–1.7 (Fig 3C) and even greater killing at 500 ppm HSP. Biofilms were exposed to biocide for only 2 hrs in these experiments and it is predicted that longer exposures would be needed to eliminate the biofilm. Others have shown an 85% reduction in P. aeruginosa biofilms with 1% H2O2 alone [57] In the field, biofilms are made of mixed microbial communities [58–61] and it is well established these adherent communities are more resistant to disinfection than planktonic bacteria [58, 61]. Treatment of established biofilms with H2O2 and H2O2/silver combinations has been shown to alter the total numbers of organisms within a biofilm [62] and to also significantly alter the diversity of organisms [63] but this study did not quantify the organisms present after different biocide treatments.

The kill curves generated with 106 CFU/mL E. coli in the presence of HSP and H2O2 showed a pronounced difference indicating that HSP was much more effective than H2O2 (Fig 1A and 1B). Several possibilities exist for this difference. It has been proposed that addition of silver to H2O2 serves to stabilize H2O2, allowing higher efficacy through increased residual levels of H2O2 [18, 20, 62]. It may be that HSP is not as effective in inducing an oxidative stress response as H2O2 and, therefore, there are higher levels of catalase secreted in response to H2O2 that serve to neutralize it. The oxidative stress response occurs very quickly upon exposure to H2O2 and induces high levels of catalase [47, 64]. The transcriptional regulator, OxyR, of the H2O2-induced stress response system is activated within 30 s of exposure to H2O2 and is therefore able to rapidly enhance transcription of enzymes such as catalase [64, 65]. Pedahzur et al. [18] measured gene expression using promoter-lux fusions, finding that the OxyR regulon member for catalase (katG) was induced 40-fold in the presence of H2O2 but not at all in the presence of silver or H2O2+silver, suggesting that the silver blocked H2O2-mediated OxyR induction. Alternatively, the silver component of HSP may enhance its activity over that of H2O2, either in providing additional biocidal activity or in altering the mechanism by which HSP interacts with and enters the cell. Of the promoters tested by Pedahzur et al., only grpE and dnaK, both components of the heat shock response, were found to be synergistically induced in the presence of H2O2+silver [18]. These authors posit that the synergistic activity of H2O2+silver results from damage to proteins, which then increases expression of heat shock proteins responsible for folding and/or refolding cellular proteins; the specific contribution of protein damage to biocidal activity is unknown.

In contrast to the expected differences in response between HSP and H2O2, the observed differences in response between different cell densities (103 and 106 CFU/mL) with HSP but not with H2O2 were not expected (Fig 1C). It was predicted that given the higher ratio of biocide to bacteria at low cell densities, E. coli would be killed faster at the lower cell densities with HSP, not slower. Indeed, faster killing was observed with NaOCl. In these experiments, cell aliquots were removed from the biocide-containing solution and excess catalase was quickly added in order to neutralize and prevent carry-over of biocide while the bacteria were being prepared for plating. It appeared that biocide neutralization was better at stopping killing at low cell concentrations, suggesting that the accessibility of HSP by catalase was being affected. Experiments were repeated with the addition of a centrifugation step in order to quickly separate the bacteria from the bulk of the biocide in solution followed by +/- catalase treatment of the cell pellets (Fig 2). It was hypothesized that HSP was binding to the bacterial cell surface and enhancing its killing efficacy. If this was the case, pelleting the cells away from HSP in solution would not stop the biocidal effect of the HSP, but subsequent addition of catalase to the cell pellets would. This time at low cell densities HSP-mediated killing was rapid in the absence of neutralization by catalase, suggesting that HSP was indeed sequestered by the bacterial cell. This HSP interaction appeared to be at the bacterial cell surface as the cell-associated HSP could be quickly neutralized by the addition of catalase. At high cell densities killing with HSP was the same, regardless of the addition of catalase, never reducing the bacterial population to zero (Fig 2A). This was likely a combination of less HSP available per bacterium and less effective dispersion of catalase at such high cell densities. Similar experiments using H2O2 showed no difference in killing efficacies suggesting the silver component of HSP promotes a unique interaction between HSP and the bacterial surface (Fig 2C and 2D). These experiments point to differences in the biocidal mechanism of HSP compared to H2O2.

It was hypothesized that the positively charged silver ions in HSP were attracted to the bacterial cell surface through electrostatic interactions and that this interaction would be inhibited by the addition of excess cations. To test this, E. coli were exposed to either HSP or H2O2 in the presence of increasing amounts of KCl or CaCl2. These cations were able to inhibit HSP-mediated killing, but had no effect on H2O2-mediated killing. As well, the divalent cation was more inhibitory than KCl (Table 2). While it is well known that insoluble AgCl can be formed in the presence of Cl-, much higher concentrations of Cl- than used here are necessary to precipitate silver [66]. Others have shown that metal ions such as copper decrease toxicity to silver in E. coli, the proposed mechanism being competition for sites at the bacterial cell surface [67]. A more recent series of experiments examining silver ion uptake by Holt and Bard [68] showed that in the presence of 1 μM AgNO3 approximately 40% of the silver binds to the outside of the cell, while the remainder is transported into the cell. Studies examining the effect of divalent cations on silver nanoparticle biocidal activity showed that a cation-dependent increase in nanoparticle size may have enhanced interaction with Gram negative bacteria [69]. The silver formulation in HSP does not display this enhanced activity. Although it was not determined in the current study if the added cations were directly associating with bacterial targets of silver ion interaction, the results clearly support the idea that silver in HSP promotes association of HSP with the bacterial cell.

Experiments were carried out to further explore if the silver component of HSP has biocidal activity in addition to that provided by the H2O2. In the continuous flow system used, there is a flux of bacteria at the surface of the biofilm as bacteria settle onto the surface or leave the biofilm as planktonic cells [55]. Sampling of the planktonic population at the conclusion of treatment showed a dose dependent killing effect that was significantly less with either HSP-silver or silver nitrate compared to HSP, although reductions of 12–15% in CFU’s and effects on live/dead ratios were detectable at 75–375 ppb silver (Fig 3). Silver nitrate solutions at concentrations of 100 ppb have previously been shown to inactivate planktonic P. aeruginosa, although significant killing required exposure of at least 8 hours at 24°C [26]. The toxicity of Ag+ is proposed to be due to several mechanisms. Several studies have shown that exposure of E. coli to silver nitrate results in a transient stimulation of respiration that is a consequence of the uncoupling of respiration from ATP synthesis [21, 68, 70, 71]. Studies have pointed to NADH dehydrogenase as the target of silver ion damage [21, 68], although additional cytoplasmic membrane protein targets are highly likely. Ultimately the induced increase in respiration results in superoxide and hydroxyl radical formation that further damages the cell [21, 68, 70]. Alteration of microbial proteins, both at the cell surface and internally has also been proposed [72], and is supported by early observations of silver-mediated induction of the heat shock response [18]. In order to demonstrate silver toxicity, many studies carried out by others used concentrations of ionic silver that were substantially higher than that used in the current study [19, 22, 67]. Given the low concentration of silver in HSP, unless the concentration of HSP in use is 500 ppm or higher, the results presented here indicate that the majority of the biocidal effects will be mediated through a synergism between H2O2 and silver activity rather than silver toxicity.

This study has conclusively shown that HSP displays significant biocidal activity towards several Gram positive and negative bacteria that are capable of producing significant levels of peroxide-neutralizing catalase. While the exact mechanism of HSP killing is still unknown, the data suggests that the silver component of HSP helps target HSP to the bacterial cell surface, thereby creating high local concentrations of H2O2. The mechanism of action of combinations of silver and H2O2 have not been clearly elucidated for either ionic or nanoparticle forms of silver [19]. It has been proposed that the addition of silver helps to stabilize the highly labile H2O2, thereby enhancing the residual levels of H2O2 and this effect has been noted with HSP (unpublished data). Several studies as discussed above noted a synergistic effect of combined silver and H2O2. It is unlikely that this synergism is a chemical effect of silver on H2O2 as the addition of ionic silver has also potentiated the activity of a variety of antimicrobials [73, 74] or metals [18]. While it has been demonstrated in this study that HSP associates with the bacterial cell surface to a greater extent than H2O2, the specific mechanism contributing to HSP efficacy remains to be determined. In addition, further studies such as those directed at understanding how organics and inorganics impact HSP efficacy in the field, as well as determining mechanisms mediating reduction of chlorination by products will significantly add to the knowledge base relating to the use of HSP in water disinfection.


We thank SanEcoTec for their assistance and provision of HSP and HSP-silver. We also thank Ashley Graveline and Jerry Liu for technical assistance.

Funding Statement

Funding was provided by two federal programs:Natural Sciences and Engineering Research Council (Canada) and Engage Program FedDev Ontario ARC (Canada). Supplies of the new generation peroxide were provided by: SanEcoTec. The funding agency did not play any role in the design, data collection and analysis, decision to publish or preparation of the manuscript. The authors regularly discussed the progress of the work with SanEcoTec and they provided a copy of the draft manuscript for review of statements of fact. They did not design, collect data, analyze or contribute to the preparation of the manuscript.Funding was provided by two federal programs:Natural Sciences and Engineering Research Council (Canada) and Engage Program FedDev Ontario ARC (Canada). Supplies of the new generation peroxide were provided by: SanEcoTec. The funding agency did not play any role in the design, data collection and analysis, decision to publish or preparation of the manuscript. The authors regularly discussed the progress of the work with SanEcoTec and they provided a copy of the draft manuscript for review of statements of fact. They did not design, collect data, analyze or contribute to the preparation of the manuscript.Funding was provided by two federal programs:Natural Sciences and Engineering Research Council (Canada) and Engage Program FedDev Ontario ARC (Canada). Supplies of the new generation peroxide were provided by: SanEcoTec. The funding agency did not play any role in the design, data collection and analysis, decision to publish or preparation of the manuscript. The authors regularly discussed the progress of the work with SanEcoTec and they provided a copy of the draft manuscript for review of statements of fact. They did not design, collect data, analyze or contribute to the preparation of the manuscript.

Data Availability

All data are publicly accessible and have been deposited at Scholars Portal Dataverse Network ( (Martin, Nancy, Bass, Paul, Liss, Steven, 2015, "Replication data for: Antibacterial Properties and Mechanism of Activity of a Novel Silver-stabilized Hydrogen Peroxide", V3 [Version]). The global id is hdl:10864/10974 and the link to the data directly is


1. White GC. The handbook of chlorination and alternative disinfectants. 4th ed: John Wiley & Sons; 1999. [Google Scholar]

2. Schoenen D. Role of disinfection in suppressing the spread of pathogens with drinking water: possibilities and limitations. Water research. 2002;36(15):3874–88. 10.1016/S0043-1354(02)00076-3 [PubMed] [CrossRef] [Google Scholar]

3. Szewzyk U, Szewzyk R, Manz W, Schleifer K-H. Microbiological safety of drinking water. Annual Review of Microbiology. 2000;54(1):81–127. 10.1146/annurev.micro.54.1.81 . [PubMed] [CrossRef] [Google Scholar]

4. Florentin A, Hautemanière A, Hartemann P. Health effects of disinfection by-products in chlorinated swimming pools. International Journal of Hygiene and Environmental Health. 2011;214(6):461–9. 10.1016/j.ijheh.2011.07.012 [PubMed] [CrossRef] [Google Scholar]

5. Richardson SD, Plewa MJ, Wagner ED, Schoeny R, DeMarini DM. Occurrence, genotoxicity, and carcinogenicity of regulated and emerging disinfection by-products in drinking water: A review and roadmap for research. Mutation Research/Reviews in Mutation Research. 2007;636(1–3):178–242. 10.1016/j.mrrev.2007.09.001 [PubMed] [CrossRef] [Google Scholar]

6. Richardson SD. Disinfection by-products and other emerging contaminants in drinking water. TrAC Trends in Analytical Chemistry. 2003;22(10):666–84. 10.1016/S0165-9936(03)01003-3 [CrossRef] [Google Scholar]

7. Smith EM, Plewa MJ, Lindell CL, Richardson SD, Mitch WA. Comparison of byproduct formation in waters treated with chlorine and iodine: Relevance to point-of-use treatment. Environmental Science & Technology. 2010;44(22):8446–52. 10.1021/es102746u [PubMed] [CrossRef] [Google Scholar]

8. Szabo J, Minamyer S. Decontamination of biological agents from drinking water infrastructure: A literature review and summary. Environment International. 2014;72(0):124–8. 10.1016/j.envint.2014.01.031 [PubMed] [CrossRef] [Google Scholar]

9. Flemming HC. Biofouling in water systems—cases, causes and countermeasures. Applied Microbiology and Biotechnology. 2002;59(6):629–40. 10.1007/s00253-002-1066-9 [PubMed] [CrossRef] [Google Scholar]

10. Juven BJ, Pierson MD. Antibacterial effects of hydrogen peroxide and methods for its detection and quantitation. Journal of Food Protection. 1996;59(11):1233–41. WOS:A1996VW02900017. [Google Scholar]

11. Baldry MG. The bactericidal, fungicidal and sporicidal properties of hydrogen peroxide and peracetic acid. The Journal of applied bacteriology. 1983;54(3):417–23. . [PubMed] [Google Scholar]

12. Vatansever F, de Melo WC, Avci P, Vecchio D, Sadasivam M, Gupta A, et al. Antimicrobial strategies centered around reactive oxygen species—bactericidal antibiotics, photodynamic therapy, and beyond. FEMS Microbiol Rev. 2013;37(6):955–89. 10.1111/1574-6976.12026 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

13. Mishra S, Imlay J. Why do bacteria use so many enzymes to scavenge hydrogen peroxide? Archives of Biochemistry and Biophysics. 2012;525(2):145–60. 10.1016/ [PMC free article] [PubMed] [CrossRef] [Google Scholar]

14. Park S, You X, Imlay JA. Substantial DNA damage from submicromolar intracellular hydrogen peroxide detected in Hpx- mutants of Escherichia coli. Proc Natl Acad Sci U S A. 2005;102(26):9317–22. 10.1073/pnas.0502051102 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

15. Walling C. Fenton's reagent revisited. Accounts of Chemical Research. 1975;8:125–31. [Google Scholar]

16. Schel AJ, Marsh PD, Bradshaw DJ, Finney M, Fulford MR, Frandsen E, et al. Comparison of the efficacies of disinfectants to control microbial contamination in dental unit water systems in general dental practices across the European Union. Applied and environmental microbiology. 2006;72(2):1380–7. 10.1128/AEM.72.2.1380-1387.2006. PMC1392914. [PMC free article] [PubMed] [CrossRef] [Google Scholar]

17. Pedahzur R, Lev O, Fattal B, Shuval HI. The interaction of silver ions and hydrogen-peroxide in the inactivation of Escherichia coli—a preliminary evaluation of a new long-acting residual drinking-water disinfectant. Water Science and Technology. 1995;31(5–6):123–9. 10.1016/0273-1223(95)00252-i. WOS:A1995RF87300023. [CrossRef] [Google Scholar]

18. Pedahzur R, Shuval HI, Ulitzur S. Silver and hydrogen peroxide as potential drinking water disinfectants: Their bactericidal effects and possible modes of action. Water Science and Technology. 1997;35(11–12):87–93. 10.1016/s0273-1223(97)00240-0. WOS:A1997XV49500017. [CrossRef] [Google Scholar]

19. Davoudi M, Ehrampoush M, Vakili T, Absalan A, Ebrahimi A. Antibacterial effects of hydrogen peroxide and silver composition on selected pathogenic enterobacteriaceae2012 January 1, 2012. 23- p. [Google Scholar]

20. Nabizadeh R, Samadi N, Sadeghpour Z, Beikzadeh M. Feasibility study of using complex of hydrogen peroxide and silver for disinfecting swimming pool water and its environment. Iranian Journal of Environmental Health Science and Engineering. 2008;5(4):235–42. [Google Scholar]

21. Maillard J-Y, Hartemann P. Silver as an antimicrobial: facts and gaps in knowledge. Critical Reviews in Microbiology. 2013;39(4):373–83. 10.3109/1040841X.2012.713323 . [PubMed] [CrossRef] [Google Scholar]

22. Slawson RM, Van Dyke MI, Lee H, Trevors JT. Germanium and silver resistance, accumulation, and toxicity in microorganisms. Plasmid. 1992;27(1):72–9. 10.1016/0147-619X(92)90008-X [PubMed] [CrossRef] [Google Scholar]

23. Tugulea AM, Bérubé D, Giddings M, Lemieux F, Hnatiw J, Priem J, et al. Nano-silver in drinking water and drinking water sources: stability and influences on disinfection by-product formation. Environ Sci Pollut Res. 2014;21(20):11823–31. 10.1007/s11356-014-2508-5 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

24. Loo S-L, Fane AG, Lim T-T, Krantz WB, Liang Y-N, Liu X, et al. Superabsorbent Cryogels Decorated with Silver Nanoparticles as a Novel Water Technology for Point-of-Use Disinfection. Environmental Science & Technology. 2013;47(16):9363–71. 10.1021/es401219s [PubMed] [CrossRef] [Google Scholar]

25. Ehdaie B, Krause C, Smith JA. Porous Ceramic Tablet Embedded with Silver Nanopatches for Low-Cost Point-of-Use Water Purification. Environmental Science & Technology. 2014;48(23):13901–8. 10.1021/es503534c [PubMed] [CrossRef] [Google Scholar]

26. Silvestry-Rodriguez N, Bright KR, Uhlmann DR, Slack DC, Gerba CP. Inactivation of Pseudomonas aeruginosa and Aeromonas hydrophila by silver in tap water. J Environ Sci Health Part A-Toxic/Hazard Subst Environ Eng. 2007;42(11):1579–84. 10.1080/10934520701517689. WOS:000249866100006. [PubMed] [CrossRef] [Google Scholar]

27. Berry D, Xi C, Raskin L. Microbial ecology of drinking water distribution systems. Current Opinion in Biotechnology. 2006;17(3):297–302. 10.1016/j.copbio.2006.05.007 [PubMed] [CrossRef] [Google Scholar]

28. Shuval H, Yarom R, Shenman R. An innovative method for the control of legionella infections in the hospital hot water systems with a stabilized hydrogen peroxide-silver formulation. International Journal of Infection Control. 2009;5(1). [Google Scholar]

29. World Health Organization. Guidelines for Drinking Water Quality. 1. 3rd ed Geneva, Switzerland: World Health Organization; 2004. p. 237–9; 433–4. [Google Scholar]

30. Roam Technology. Available: Accessed 01 December 2014.

31. Linley E, Denyer SP, McDonnell G, Simons C, Maillard J-Y. Use of hydrogen peroxide as a biocide: new consideration of its mechanisms of biocidal action. Journal of Antimicrobial Chemotherapy. 2012;67(7):1589–96. 10.1093/jac/dks129 [PubMed] [CrossRef] [Google Scholar]

32. Kim M-J. The effect of sludge retention time on dewaterability of activated sludge [M.A.Sc]: University of Toronto; 2001. [Google Scholar]

33. Steiner AA, van Winden H. Recipe for ferric salts of ethylenediaminetetraacetic Acid. Plant physiology. 1970;46(6):862–3. [PMC free article] [PubMed] [Google Scholar]

34. Vianna ME, Gomes BP, Berber VB, Zaia AA, Ferraz CC, de Souza-Filho FJ. In vitro evaluation of the antimicrobial activity of chlorhexidine and sodium hypochlorite. Oral surgery, oral medicine, oral pathology, oral radiology, and endodontics. 2004;97(1):79–84. 10.1016/S1079210403003603 . [PubMed] [CrossRef] [Google Scholar]

35. Andrews JM. Determination of minimum inhibitory concentrations. The Journal of antimicrobial chemotherapy. 2001;48 Suppl 1:5–16. . [PubMed] [Google Scholar]

36. Kroukamp O, Wolfaardt GM. CO2 production as an indicator of biofilm metabolism. Applied and environmental microbiology. 2009;75(13):4391–7. 10.1128/AEM.01567-08 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

37. Smaill F. Antibiotic susceptibility and resistance testing: An overview. Canadian Journal of Gastroenterology & Hepatology. 2000;14(10):871–5. [PubMed] [Google Scholar]

38. Imlay JA. The molecular mechanisms and physiological consequences of oxidative stress: lessons from a model bacterium. Nature reviews Microbiology. 2013;11(7):443–54. 10.1038/nrmicro3032. PMC4018742. [PMC free article] [PubMed] [CrossRef] [Google Scholar]

39. Fernandes P, Mannarino SC, Silva CG, Pereira MD, Panek AD, Eleutherio ECA. Oxidative stress response in eukaryotes: effect of glutathione, superoxide dismutase and catalase on adaptation to peroxide and menadione stresses in Saccharomyces cerevisiae. Redox Report. 2007;12(5):236–44. 10.1179/135100007X200344 . [PubMed] [CrossRef] [Google Scholar]

40. Winter J, Ilbert M, Graf PCF, Özcelik D, Jakob U. Bleach activates a redox-regulated chaperone by oxidative protein unfolding. Cell. 2008;135(4):691–701. 10.1016/j.cell.2008.09.024. PMC2606091. [PMC free article] [PubMed] [CrossRef] [Google Scholar]

41. Committee NRCUSDW. Drinking water and health, disinfectants and disinfectant by-products. Washington, DC: The National Academies Press; 1987. 212 p. [Google Scholar]

42. Bonvillain RW, Painter RG, Ledet EM, Wang G. Comparisons of resistance of CF and non-CF pathogens to hydrogen peroxide and hypochlorous acid oxidants in vitro. BMC Microbiol. 2011;11:112 10.1186/1471-2180-11-112 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

43. Kumari P, Kamiseki M, Biyani M, Suzuki M, Nemoto N, Aita T, et al. Detection of ultra-low levels of DNA changes by drinking water: epidemiologically important finding. Journal of Biochemistry. 2014. 10.1093/jb/mvu072 [PubMed] [CrossRef] [Google Scholar]

44. Sadiq R, Rodriguez MJ. Disinfection by-products (DBPs) in drinking water and predictive models for their occurrence: a review. Science of The Total Environment. 2004;321(1–3):21–46. 10.1016/j.scitotenv.2003.05.001 [PubMed] [CrossRef] [Google Scholar]

45. Munoz M, de Pedro ZM, Casas JA, Rodriguez JJ. Assessment of the generation of chlorinated byproducts upon Fenton-like oxidation of chlorophenols at different conditions. Journal of Hazardous Materials. 2011;190(1–3):993–1000. 10.1016/j.jhazmat.2011.04.038 [PubMed] [CrossRef] [Google Scholar]

46. Fu F, Dionysiou DD, Liu H. The use of zero-valent iron for groundwater remediation and wastewater treatment: A review. Journal of Hazardous Materials. 2014;267(0):194–205. 10.1016/j.jhazmat.2013.12.062 [PubMed] [CrossRef] [Google Scholar]

47. Seaver LC, Imlay JA. Hydrogen peroxide fluxes and compartmentalization inside growing Escherichia coli. J Bacteriol. 2001;183(24):7182–9. 10.1128/JB.183.24.7182-7189.2001 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

48. Brown SM, Howell ML, Vasil ML, Anderson AJ, Hassett DJ. Cloning and characterization of the katB gene of Pseudomonas aeruginosa encoding a hydrogen peroxide-inducible catalase: purification of KatB, cellular localization, and demonstration that it is essential for optimal resistance to hydrogen peroxide. Journal of Bacteriology. 1995;177(22):6536–44. PMC177506. [PMC free article] [PubMed] [Google Scholar]

49. Ochsner UA, Vasil ML, Alsabbagh E, Parvatiyar K, Hassett DJ. Role of the Pseudomonas aeruginosa oxyR-recG operon in oxidative stress defense and dna repair: OxyR-dependent regulation of katB-ankB, ahpB, and ahpC-ahpF. Journal of Bacteriology. 2000;182(16):4533–44. PMC94625. [PMC free article] [PubMed] [Google Scholar]

50. Hare NJ, Scott NE, Shin EHH, Connolly AM, Larsen MR, Palmisano G, et al. Proteomics of the oxidative stress response induced by hydrogen peroxide and paraquat reveals a novel AhpC-like protein in Pseudomonas aeruginosa. PROTEOMICS. 2011;11(15):3056–69. 10.1002/pmic.201000807 [PubMed] [CrossRef] [Google Scholar]

51. Loewen PC, Switala J. Multiple catalases in Bacillus subtilis. Journal of Bacteriology. 1987;169(8):3601–7. PMC212438. [PMC free article] [PubMed] [Google Scholar]

52. Mulvey MR, Sorby PA, Triggs-Raine BL, Loewen PC. Cloning and physical characterization of katE and katF required for catalase HPII expression in Escherichia coli. Gene. 1988;73(2):337–45. 10.1016/0378-1119(88)90498-2 [PubMed] [CrossRef] [Google Scholar]

53. Triggs-Raine BL, Loewen PC. Physical characterization of katG, encoding catalase HPI of Escherichia coli. Gene. 1987;52(2–3):121–8. 10.1016/0378-1119(87)90038-2 [PubMed] [CrossRef] [Google Scholar]

54. Cosgrove K, Coutts G, Jonsson I-M, Tarkowski A, Kokai-Kun JF, Mond JJ, et al. Catalase (KatA) and Alkyl Hydroperoxide Reductase (AhpC) Have Compensatory Roles in Peroxide Stress Resistance and Are Required for Survival, Persistence, and Nasal Colonization in Staphylococcus aureus. Journal of Bacteriology. 2007;189(3):1025–35. 10.1128/JB.01524-06. PMC1797328. [PMC free article] [PubMed] [CrossRef] [Google Scholar]

55. Bester E, Kroukamp O, Wolfaardt GM, Boonzaaier L, Liss SN. Metabolic differentiation in biofilms as indicated by carbon dioxide production rates. Applied and environmental microbiology. 2010;76(4):1189–97. 10.1128/AEM.01719-09 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

56. Kroukamp O, Dumitrache RG, Wolfaardt GM. Pronounced effect of the nature of the inoculum on biofilm development in flow systems. Applied and environmental microbiology. 2010;76(18):6025–31. 10.1128/AEM.00070-10 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

57. Tote K, Horemans T, Vanden Berghe D, Maes L, Cos P. Inhibitory effect of biocides on the viable masses and matrices of Staphylococcus aureus and Pseudomonas aeruginosa biofilms. Applied and environmental microbiology. 2010;76(10):3135–42. 10.1128/AEM.02095-09 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

58. Emtiazi F, Schwartz T, Marten SM, Krolla-Sidenstein P, Obst U. Investigation of natural biofilms formed during the production of drinking water from surface water embankment filtration. Water research. 2004;38(5):1197–206. 10.1016/j.watres.2003.10.056 [PubMed] [CrossRef] [Google Scholar]

59. Wingender J, Flemming H-C. Biofilms in drinking water and their role as reservoir for pathogens. International Journal of Hygiene and Environmental Health. 2011;214(6):417–23. 10.1016/j.ijheh.2011.05.009 [PubMed] [CrossRef] [Google Scholar]

60. Schwartz T, Hoffmann S, Obst U. Formation and bacterial composition of young, natural biofilms obtained from public bank-filtered drinking water systems. Water research. 1998;32(9):2787–97. 10.1016/S0043-1354(98)00026-8 [CrossRef] [Google Scholar]

61. Liu G, Verberk JQJC, Van Dijk JC. Bacteriology of drinking water distribution systems: an integral and multidimensional review. Applied Microbiology and Biotechnology. 2013;97(21):9265–76. 10.1007/s00253-013-5217-y [PubMed] [CrossRef] [Google Scholar]

62. Armon R, Laot N, Lev O, Shuval H, Fattal B. Controlling biofilm formation by hydrogen peroxide and silver combined disinfectant. Water Science & Technology. 2000;42(1/2):187–92. . [Google Scholar]

63. Roeder RS, Lenz J, Tarne P, Gebel J, Exner M, Szewzyk U. Long-term effects of disinfectants on the community composition of drinking water biofilms. International Journal of Hygiene and Environmental Health. 2010;213(3):183–9. 10.1016/j.ijheh.2010.04.007 [PubMed] [CrossRef] [Google Scholar]

64. Pomposiello PJ, Demple B. Redox-operated genetic switches: the SoxR and OxyR transcription factors. Trends in Biotechnology. 2001;19(3):109–14. 10.1016/S0167-7799(00)01542-0 [PubMed] [CrossRef] [Google Scholar]

65. Tao K. In vivo oxidation-reduction kinetics of OxyR, the transcriptional activator for an oxidative stress-inducible regulon in Escherichia coli. FEBS Letters. 1999;457(1):90–2. 10.1016/S0014-5793(99)01013-3 [PubMed] [CrossRef] [Google Scholar]

66. Gadd GM, Laurence OS, Briscoe PA, Trevors JT. Silver accumulation in Pseudomonas stutzeri AG259. Biology of metals. 1989;2(3):168–73. . [PubMed] [Google Scholar]

67. Ghandour W, Hubbard JA, Deistung J, Hughes MN, Poole RK. The uptake of silver ions by Escherichia-coli-K12—toxic effects and interaction with copper ions. Applied Microbiology and Biotechnology. 1988;28(6):559–65. WOS:A1988P180300009. [Google Scholar]

68. Holt KB, Bard AJ. Interaction of silver(i) ions with the respiratory chain of Escherichia coli: An electrochemical and scanning electrochemical microscopy study of the antimicrobial mechanism of micromolar Ag+. Biochemistry. 2005;44(39):13214–23. 10.1021/bi0508542 [PubMed] [CrossRef] [Google Scholar]

69. Jin X, Li M, Wang J, Marambio-Jones C, Peng F, Huang X, et al. High-throughput screening of silver nanoparticle stability and bacterial inactivation in aquatic media: Influence of specific ions. Environmental Science & Technology. 2010;44(19):7321–8. 10.1021/es100854g [PubMed] [CrossRef] [Google Scholar]

70. Yudkin J. Effect of silver ions on enzymes of bacterium coli. Enzymologia. 1937;2:161–70. [Google Scholar]

71. Bragg PD, Rainnie DJ. The effect of silver ions on the respiratory chain of Escherichia coli. Can J Microbiol. 1974;20(6):883–9. . [PubMed] [Google Scholar]

72. Silver S, Phung LT, Silver G. Silver as biocides in burn and wound dressings and bacterial resistance to silver compounds. Journal of Industrial Microbiology & Biotechnology. 2006;33(7):627–34. 10.1007/s10295-006-0139-7 [PubMed] [CrossRef] [Google Scholar]

73. Batarseh KI, Smith MA. Synergistic activities of a silver(i) glutamic acid complex and reactive oxygen species (ros): A novel antimicrobial and chemotherapeutic agent. Current Medicinal Chemistry. 2012;19(21):3635–40. WOS:000305946800013. [PubMed] [Google Scholar]

74. Morones-Ramirez JR, Winkler JA, Spina CS, Collins JJ. Silver enhances antibiotic activity against gram-negative bacteria. Science Translational Medicine. 2013;5(190):190ra81 10.1126/scitranslmed.3006276 [PMC free article] [PubMed] [CrossRef] [Google Scholar]

Bespoke Equine Testing

We have gone to the very well respected equine laboratory of the Irish Equine Centre to have additional efficacy testing carried out. 

We have commissioned testing done to unusually low contact times across various dilution rates. These tests were carried out using an equine serum as an interfering agent under clean and dirty conditions