- Open Access
Assessing the phytotoxicity of cetrimonium bromide in plants using eco-physiological parameters
© The Author(s) 2016
Received: 11 May 2016
Accepted: 31 August 2016
Published: 24 November 2016
Although cetrimonium bromide is widely used for its bactericidal effects, the safety of cetrimonium bromide remains controversial. Therefore, the phytotoxicity of cetrimonium bromide was tested to evaluate its acute toxicity to plants and possible toxicity to other organisms and the ecosystem.
The germination rates of two test species, Lactuca sativa and Brassica campestris, were significantly decreased after cetrimonium bromide treatment. Furthermore, cetrimonium bromide treatment at over 1 mg/L concentration significantly affected root elongation immediately after germination. In pot experiments with semi-mature plants, significantly decreased shoot elongation and chlorophyll content were detected in both species following cetrimonium bromide treatment. Cetrimonium bromide treatment also significantly increased the antioxidant enzyme activities of plants.
Our results show that cetrimonium bromide is phytotoxic, and since phytotoxicity testing can imply potential toxicity in the environment, further studies of the environmental toxicity of cetrimonium bromide should be performed.
Cetrimonium bromide, (C16H33)N(CH3)3Br (CAS no. 57-09-0), also known as hexadecyl-trimethyl-ammonium bromide (International Union of Pure and Applied Chemistry [IUPAC] name), is an amine-based cationic quaternary surfactant that is widely used in components of antiseptic materials (Andersen 1997). Cetrimonium bromide is used in hygienic goods and cleaning agents for bactericidal effects (Oh et al. 2014) and in many cosmetics. However, recently there has been much debate about the safety of cetrimonium bromide (Woo 2015). Since cetrimonium bromide, which was present in many cosmetic products, was believed to be associated with human disease, the safety of this chemical has been questioned (Kim 2014). Furthermore, cetrimonium bromide is used in baby wet tissue wipes, resulting in much debate on its safety (Woo 2015). However, despite these problems, there are a very limited number of studies on the toxicity of this chemical. Among the few studies, one research group reported an increase in fetal deaths in mice treated with 35.0 mg/kg cetrimonium bromide, although other studies of cetrimonium bromide did not show any acute toxicity (Andersen 1997). However, as there are only a few reports, further studies are required to determine the acute toxicity of cetrimonium bromide. Moreover, although cetrimonium bromide is commonly believed to be dangerous for the environment, especially in aquatic ecosystems, the toxicity of cetrimonium bromide to aquatic organisms is not well documented (Tišler et al. 2004). Therefore, further research on the ecotoxicity of cetrimonium bromide is required.
Phytotoxicity testing is often used to estimate potential toxicity in the environment and for risk assessment of chemicals and formulations of human relevance (Kristen 1997). Phytotoxicity tests are relatively simple but precise toxicological assays with sensitive results (Kristen 1997). Since the toxicity of cetrimonium bromide is still undetermined and its ecotoxicity is almost unknown, testing the toxicity of cetrimonium bromide with plants would supply further information on the toxicity and ecotoxicity of cetrimonium bromide. Therefore, in this study, the phytotoxicity of cetrimonium bromide was tested by evaluating seed germination rates, root elongation, and the ecophysiological responses of mature vegetable crops.
Cetrimonium bromide was purchased from Daejung Chemicals and Materials (Daejung C&M, Gyonggi Province, Korea). The purity was above 99%, and loss on drying at 100 °C was less than 2%. We used 0.01 mg/L, 0.1 mg/L, 1 mg/L, 10 mg/L, 100 mg/L, and 1000 mg/L cetrimonium bromide solutions for testing by adding measured weight of cetrimonium bromide to distilled water. Although cetrimonium bromide is used at up to 10% concentration in cosmetics (Andersen 1997), we tested up to 1000 mg/L because animal toxicity was observed at a 10 mg/L concentration (Andersen 1997), and concentrations of approximately 29 mg/L can be found in wet tissues (Oh et al. 2014). Therefore, 0.01 mg/L, 0.1 mg/L, and 1 mg/L treatments were selected for testing of environmentally realistic concentrations, and 10 mg/L, 100 mg/L, and 1000 mg/L treatments were selected to test acute toxicity.
Seeds of Brassica campestris ssp. napus var. nippo-oleifera Makina (oilseed rape) and Lactuca sativa L. (lettuce) were selected to test the toxicity of cetrimonium bromide. These species were selected because they are common, easy to obtain, and included among the species recommended for the testing of chemicals in the Organisation for Economic Co-operation and Development guidelines (OECD, 2003). Seeds were purchased from a local Syngenta agent (Syngenta AG, Switzerland). The seeds were vernalized for 2 weeks and sterilized for 10 min in 10% sodium hypochlorite solution (USEPA, 1996) before application.
For germination rate tests, seeds were soaked in cetrimonium bromide solutions for 24 h (Zheng et al. 2005) in the dark at room temperature with gentle shaking on an orbital shaker at 60 rpm to improve mixing. Subsequently, the seeds were washed with distilled water. Most seeds were transferred to 100-mm Petri dishes containing a piece of filter paper (90 mm) and 6 mL of distilled water (Lin and Xing 2007). The seeds were tested for germination in a growth chamber under a range of conditions established by the OECD guidelines (OECD, 2003): temperature 25 °C, humidity 70 ± 25%, photoperiod 18 h light, light intensity 300 μE · m−2 · s−1 with protection from drying. Each Petri dish (n = 5) contained five seeds, and germination rates were investigated for 1 week.
For root elongation studies, seeds were germinated in Petri dishes. After 2 days, germinated seeds were moved to new Petri dishes. Each Petri dish contained five seedlings and 5 mL of the test medium (n = 3). The root lengths of the seedlings were measured every 3 days (six times altogether). Other conditions, including solution concentrations and chamber conditions, were the same as those of the germination study, described above.
For pot experiment, plants were germinated and grown in a 50-hole pot tray with each hole filled with 10 g of commercial growing soil (Pro-100, Chamgrow, Korea). After a 5-week growing period from the seedling stage, 10 mL of cetrimonium bromide solution was added to each pot (0.01 mg/L, 0.1 mg/L, 1 mg/L, 10 mg/L, 100 mg/L, and 1000 mg/L; seven replicates for each treatment). Solutions were administered several times with a 1-mL pipette to avoid leaching. Therefore, the growing soil contained exactly 0.01 mg/kg, 0.1 mg/kg, 1 mg/kg, 10 mg/kg, 100 mg/kg, and 1000 mg/kg of cetrimonium bromide. The chlorophyll content of leaves was measured using a SPAD 502 system (Minolta Co., Japan), 1 week after treatment. The antioxidant enzyme activities (total antioxidant capacity [TAC] and superoxide dismutase [SOD] activity) of the plants were measured using the protocols of Song and Lee, 2010, 1 week after treatment (five replicates). The average height of the shoots of the plants was 6.4 ± 0.5 cm for Lactuca sativa, and 6.7 ± 0.3 cm for Brassica campestris (values represent mean ± SE of 49 replicates). Plant growth after treatment was also measured for 1 week.
A one-way ANOVA was performed to identify significant differences between treatments. Upon detection of a significant difference, Tukey’s studentized range (honest significant difference) test was applied post hoc and assessed using SAS 9.3 software (SAS Institute Inc., USA). Differences were considered significant when p < 0.05.
Results and discussion
Germination rates (%) of plants after cetrimonium bromide treatment
98.0 ± 2.0a
100.0 ± 0.0a
96.0 ± 2.4a
98.0 ± 2.0a
96.0 ± 2.4a
100.0 ± 0.0a
86.0 ± 2.4ab
86.0 ± 2.4ab
88.0 ± 5.8a
92.0 ± 4.9a
74.0 ± 5.1abc
78.0 ± 4.9ab
86.0 ± 2.4a
92.0 ± 3.7a
74.0 ± 6.0abc
76.0 ± 5.1ab
86.0 ± 5.1a
92.0 ± 3.7a
72.0 ± 5.8bc
76.0 ± 7.5ab
46.0 ± 6.8b
54.0 ± 6.8b
72.0 ± 4.9bc
76.0 ± 5.1ab
0.0 ± 0.0c
0.0 ± 0.0c
64.0 ± 6.8c
66.0 ± 6.8b
Shoot elongation (mm) of plants 1 week after cetrimonium bromide treatment
3.4 ± 0.6ab
8.1 ± 1.7ab
3.3 ± 0.7abc
10.1 ± 1.7a
3.7 ± 1.0a
5.0 ± 1.5ab
1.0 ± 0.2bcd
5.0 ± 1.7ab
1.3 ± 0.2abcd
6.8 ± 2.1ab
0.8 ± 0.3cd
1.8 ± 0.8b
0.0 ± 0.0d
0.2 ± 0.1c
Chlorophyll content (SPAD-502 units) of plant leaves 1 week after cetrimonium bromide treatment
14.2 ± 0.2a
23.2 ± 1.1a
11.2 ± 0.3b
21.5 ± 0.3ab
10.2 ± 0.3bc
18.8 ± 0.3bc
9.3 ± 0.4c
17.2 ± 0.8c
9.4 ± 0.2c
16.7 ± 0.6c
7.0 ± 0.3d
11.5 ± 0.7d
4.4 ± 0.5e
6.8 ± 0.9e
Zinc accumulation in plants after exposure to zinc oxide nanoparticles for 5 weeks
Zinc content (mg/kg)
0.02 ± 0.01c
0.08 ± 0.01c
0.22 ± 0.01c
0.10 ± 0.01c
0.57 ± 0.31bc
0.11 ± 0.01c
1.17 ± 0.03ab
0.20 ± 0.03b
1.43 ± 0.03a
0.35 ± 0.01a
1.47 ± 0.03a
0.34 ± 0.01a
1.67 ± 0.22a
Chlorophyll content was more sensitive to treatment, as both plant species showed significantly decreased chlorophyll content even at the lowest (0.01 mg/kg) concentration (Table 3). Especially with treatments over 100 mg/kg in concentration, both species lost chlorophyll and began to fade. As the environmentally realistic treatments all resulted in significantly decreased chlorophyll content, cetrimonium bromide will likely affect plants in the field when it is released into the surrounding environment (ecosystem).
Notably, these results indicate that when the cetrimonium bromide used by humans enters aquatic ecosystems via sewage, the impact on aquatic plants could be considerable, and therefore the results should be monitored and investigated. The original experimental design intended to monitor plant growth and chlorophyll content for a few weeks, but since the plants treated at high concentrations began to fade and lose chlorophyll within 1 week (Table 3), we harvested the plants for antioxidant enzyme activity assays before the plants died. Table 4 shows the antioxidant enzyme activities of Lactuca sativa after cetrimonium bromide treatment. We intended to measure the antioxidant enzyme activities of both species; however, there was not enough Brassica campestris leaf biomass (over 1 g fresh weight) for protein extraction via a phosphate buffer and Bradford assay (Song and Lee 2010). The above ground biomass allocation of Brassica campestris was over 75% on stems, even in the control, and there was not enough leaf biomass. Cetrimonium bromide treatment significantly increased both the TAC and SOD values (Table 4), indicating that the plants were under stress (Song, Jun, et al. 2013). The TAC results in particular indicate that the plants were under overall stress, which may be reflected in the growth and chlorophyll content of the plants (Tables 2 and 3). SOD values are frequently used as an indicator of pollutant stress (Koricheva et al. 1997). Since plants treated at over 0.1 mg/kg showed significantly increased SOD values, cetrimonium bromide should be treated as a potential pollutant. As bromine residues in the soil can cause phytotoxicity (Lear 1975), cetrimonium bromide clearly shows phytotoxicity. Overall, all of the above results, including the germination rate, root and shoot elongation, chlorophyll content, and antioxidant enzyme activity, consistently show that cetrimonium bromide is phytotoxic.
The germination rates of both Lactuca sativa and Brassica campestris species were significantly decreased after cetrimonium bromide treatment. Notably, both species showed total inhibition of germination with the 1000 mg/L treatment. Furthermore, cetrimonium bromide treatment significantly affected root elongation immediately after germination. In semi-mature plants, significant reductions in shoot elongation and chlorophyll content were detected in both species after cetrimonium bromide treatment. Antioxidant enzyme activities of the plants were also significantly increased by cetrimonium bromide. These results indicate that cetrimonium bromide is markedly phytotoxic. However, surprisingly there are no related articles that report the phytotoxicity of cetrimonium bromide. Since phytotoxicity testing can be used to estimate potential toxicity in the environment, our results show that cetrimonium bromide could also be toxic to other organisms and ecosystems when released into the surrounding environment. Also, as cetrimonium bromide is likely to be mostly released by hydrologic system as the chemical is mainly used for water and cosmetic treatment, the growth of vegetables also could be affected by irrigation. As only a few articles report the toxicity of cetrimonium bromide, and these are limited to human (Momblano et al. 1984) and mammal (Andersen 1997) toxicity, further studies to define the acute toxicity to other organisms and potential environmental toxicity should be performed. Furthermore, cetrimonium bromide should be carefully monitored for its effects after release into the surrounding environment and into edible crops. Therefore, further studies of the toxicity of cetrimonium bromide at both the species level and environment-ecosystem level are required.
This research was supported by the 2015 scientific promotion program funded by Jeju National University.
US designed the experiment, participated the chamber experiment and drafted the manuscript. HE participated the chamber experiment. All authors read and approved the final manuscript.
The authors declare that they have no competing interests.
Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made. The Creative Commons Public Domain Dedication waiver (http://creativecommons.org/publicdomain/zero/1.0/) applies to the data made available in this article, unless otherwise stated.
- Andersen, F. (1997). Final report on the safety assessment of cetrimonium chloride, cetrimonium bromide, and steartrimonium chloride. Int J Toxicol, 16, 195–220.View ArticleGoogle Scholar
- Kim, SJ. (2014). Stricter safety standards on wet tissues, shampoo The Korea Times. https://www.koreatimes.co.kr/www/common/printpreview.asp?categoryCode=116&newsIdx=169060.Google Scholar
- Koricheva, J, Roy, S, Vranjic, JA, Haukioja, E, Hughes, PR, & Hänninen, O. (1997). Antioxidant responses to simulated acid rain and heavy metal deposition in birch seedlings. Environ Pollut, 95, 249–258.View ArticlePubMedGoogle Scholar
- Kristen, U (1997). Use of higher plants as screens for toxicity assessment. Toxicol in Vitro, 11, 181–191.View ArticlePubMedGoogle Scholar
- Lear, B (1975). Phytotoxicity associated with bromide uptake in plants grown in soil fumigated with brominated hydrocarbon. Nematologica, 5, 24.Google Scholar
- Lin, D, & Xing, B (2007). Phytotoxicity of nanoparticles: inhibition of seed germination and root growth. Environ Pollut, 150, 243–250.View ArticlePubMedGoogle Scholar
- Momblano, P, Pradere, B, Jarrige, N, Concina, D, Bloom, E (1984). Metabolic acidosis induced by cetrimonium bromide. Lancet, 324, 1045.View ArticleGoogle Scholar
- Oh, J, Kim, K, Pyo, H, Chung, BC, Lee, J (2014). External standard addition method development of benzalkonium chloride, cetrimonium bromide and cetylpyridinium chloride in wet-tissues by liquid chromatography-electrospray ionization/mass spectrometry (pp. 232–232). Proceedings of 53th symposium of the Korean society of analytical sciences.Google Scholar
- Organization for Economic Cooperation and Development (OECD). (2003). OECD Guidelines for the testing of chemicals: Proposals for updating guideline 208 - Terrestrial Plant Test: Seedling Emergence and Seedling Growth Test. http://www.oecd.org/dataoecd/11/31/33653757.pdf.Google Scholar
- Song, U, Lee, E (2010). Ecophysiological responses of plants after sewage sludge compost applications. J Plant Biol, 53, 259–267.View ArticleGoogle Scholar
- Song, U, Jun, H, Waldman, B, Roh, J, Kim, Y, Yi, J, Lee, EJ. (2013). Functional analyses of nanoparticle toxicity: a comparative study of the effects of TiO2 and Ag on tomatoes (Lycopersicon esculentum). Ecotoxicol Environ Safety, 93, 60–67.View ArticlePubMedGoogle Scholar
- Song, U, Shin, M, Lee, G, Roh, J, Kim, Y, Lee, E (2013). Functional analysis of TiO2 nanoparticle toxicity in three plant species. Biol Trace Elem Res, 155, 93–103.View ArticlePubMedGoogle Scholar
- Song, U, Mun, S, Waldman, B, Lee, E (2014). Effects of three fire-suppressant foams on the germination and physiological responses of plants. Environ Manage, 54, 865–874.View ArticlePubMedGoogle Scholar
- Tišler, T, Zagorc-Končan, J, Cotman, M, Drolc, A (2004). Toxicity potential of disinfection agent in tannery wastewater. Water Res, 38, 3503–3510.View ArticlePubMedGoogle Scholar
- U.S. Environmental Protection Agency (USEPA). 1996. Ecological effects test guidelines (OPPTS 850.4200): Seed Germination/Root Elongation Toxicity Test. http://www.epa.gov/opptsfrs/publications/OPPTS_Harmonized/850_Ecological_Effects_Test_Guidelines/Drafts/850-4200.pdf
- Woo, HC (2015). Baby wipes raise health concerns The Korea Times. http://www.koreatimes.co.kr/www/news/biz/2014/09/123_164982.html. Accessed 21 Oct 2015.Google Scholar
- Zheng, L, Hong, F, Lu, S, Liu, C (2005). Effect of nano-TiO(2) on strength of naturally aged seeds and growth of spinach. Biol Trace Elem Res, 104, 83–91.View ArticlePubMedGoogle Scholar
- Zonno, MC, Vurro, M (2002). Inhibition of germination of Orobanche ramosa seeds by Fusarium toxins. Phytoparasitica, 30, 519–524.View ArticleGoogle Scholar