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Environmental considerations[edit]

Paraben release into the environment[edit]

Paraben discharge into the environment is common due to its ubiquitous usage in cosmetic products. A 2010 study on consumer available personal care products revealed that 44% of the tested products contain parabens [1]. When washing these products off the human body, they flow down the drain and into community wastewater. Once this occurs, the potential for parabens to accumulate within aqueous and solid mediums materializes. Some of the most common paraben derivatives found in the environment include methylparaben, ethylparaben, propylparaben, and butylparaben[2]. Parabens flow from wastewater to wastewater treatment plants (WWTP) as influent where they are either removed, chemically altered, or released into the environment through sludge or tertiary effluent[2].

General flow of parabens as they make their way through wastewater treatment plants.

In one New York WWTP, mass load of all parent paraben derivatives (methylparaben, ethylparaben, propylparaben, butylparaben, etc.) from influent wastewater was found to be 176 mg/day/1000 people [3]. When this value is used to estimate the amount of parabens entering WWTPs from the 8.5 million people currently residing in New York City for an entire year, a value of approximately 546 kg of parabens is calculated. Therefore, levels of paraben accumulation prove significant upon long-term observance. WWTPs eliminate between 92%-98% of paraben derivatives; however, much of this removal is due to the formation of degradation products[3]. Despite their reputed high elimination through WWTPs, various studies have measured high levels of paraben derivatives and degradation products persisting in the environment[4].


Formation of paraben degradation products[edit]

Chlorinated Products[edit]

In addition to parent parabens, paraben degradation products that form throughout WWTP stages present a concern to the environment, including mono- and di- chlorinated parabens. When paraben-containing products are washed down the drain, parabens have the potential to undergo chlorination reactions[5]. This reaction can occur with free chlorine present in tap water or with Sodium hypochlorite, which is often used in WWTPs as a final disinfectant step[6]. In neutral water, Raman spectroscopy has confirmed that chlorine is predominantly present as Hypochlorous acid (HClO)[7]. Parabens can react with HClO to form mono- and di- chlorinated products through Electrophilic aromatic substitution[5]. The electrophilic attack of the chlorine forms a carbocation that is stabilized by donated electron density from the hydroxyl group of the paraben[8]. This step is endergonic due to the loss of aromaticity, though the hydroxyl group acts as an activating group that increases the rate[5]. A base can then abstract a proton from the carbon containing the chlorine, which is followed by subsequent restoration of aromaticity by the involved pi electrons. Since the hydroxyl group is more activating than the ester group of the paraben, the reaction will direct in both ortho positions, as the para position is already blocked[8].

Reaction of a general paraben with hypochlorous acid (HClO) to form mono- and di- chlorinated products.
Arrow pushing mechanism of the formation of a mono-chlorinated paraben.
Arrow pushing mechanism of the formation of a mono-chlorinated paraben.

The Arrhenius equation was used in a study to calculate activation energies for the chlorination of four parent parabens (methyl-, ethyl-, propyl-, and butylparaben) and was found to range from 36 kJ/mol - 47 kJ/mol [5]. In another study, tap water at 20° Celsius containing 50 µM- 200 µM free chlorine was spiked with 0.5 µM propylparaben and the composition of the mixture was monitored over 40 minutes to determine if chlorination occurs under conditions found in tap water [6]. Results from the study confirm the disappearance of propylparaben after 5 minutes, the appearance of both 3-chloro-propylparaben and 3,5-dichloro-propylparaben paraben by 5 minutes, and the persistence of 3,5-dichloro-propylparaben as the main species remaining in the reaction [6]. A similar, though more rapid, trend was found in a study in which the reaction temperature was increased to 35° Celsius [5].

Chlorination of propylparaben over time in water at 20° Celsius containing .5 μM propylparaben and 50 μM free chlorine.
Chlorination of propylparaben over time in water at 20° Celsius containing .5 μM propylparaben and 50 μM free chlorine.

4-hydroxybenzoic acid (PHBA)[edit]

Another significant paraben degradation product includes 4-Hydroxybenzoic acid (PHBA). There are two mechanisms in which parabens can degrade to PHBA. The first degradation route occurs chemically. Parent parabens readily undergo base-catalyzed hydrolysis of the ester bond, forming PHBA. The reaction occurs under moderately alkaline conditions, specifically when the pH is ≥ 8 [5]. This reaction is quite prevalent in household environments due to the pH range of household wastewater being 6-9 [9] and the prevalent existence of parabens in cosmetic products. When paraben-containing cosmetic products are discharged into community wastewater influent, they become exposed to an environment where the pH ≥ 8, and the base-catalyzed hydrolysis of the parent paraben ensues, forming PHBA.

Overall reaction showing the degradation of a parent paraben to 4-hydroxybenzoic acid through base-catalyzed hydrolysis of the ester bond.

In the electron transfer mechanism, the pi electrons in the double bond between the oxygen and carbonyl carbon resonate to the oxygen, leaving a negative charge on the oxygen and a positive charge on the carbonyl carbon. A hydroxide ion, acting as a nucleophile, attacks the now electrophilic carbonyl carbon, yielding sp3 hybridization on the carbonyl carbon. The electrons resonate back to form the double bond between the oxygen and the carbonyl carbon. In order to retain the original sp2 hybridization, the –OR group will leave. The –OR group acts as a better leaving group than the –OH group due to its ability to maintain a negative charge with greater stability. Lastly, the –OR-, acting as a base, will deprotonate the carboxylic acid to form a carboxylate anion.

Arrow pushing mechanism showing the degradation of a parent paraben into PHBA through base-catalyzed hydrolysis of the ester bond
Arrow pushing mechanism showing the degradation of a parent paraben into PHBA through base-catalyzed hydrolysis of the ester bond

The second way in which parabens can degrade into PHBA occurs biologically within WWTPs. During the secondary clarifier phase of Wastewater treatment, sludge accumulates at the bottom of the secondary clarifier. Upon separation of the liquid and solid phases of the incoming influent, parabens have a greater tendency accumulate in the sludge. This is due to its moderate hydrophobicity, as quantified by a log Kow value of approximately 1.58[10]. This sludge is concentrated in organic nutrients; consequently, a proliferation of microorganisms becomes common within the sludge. One organism is Enterobacter cloacae, which biologically metabolizes the sludge parabens into PHBA[11].

Accumulation of paraben degradation products in the environment[edit]

Through various analytical techniques such as Gas chromatography and High-performance liquid chromatography, the exact levels of accumulation of paraben derivatives and degradation products in the environment have been quantified[2][6]. These levels have been accurately measured in tertiary effluent and sewage sludge, as these are the primary avenues for which parabens and their degradation products reach the environment upon discharge from WWTPs. [2]

Concentrations of Parabens in Tertiary Effluent Water samples in μg/L (left). Concentrations of Parabens in Sewage Sludge samples in μg/g (right).

Paraben stability in sewage sludge is relatively high due to their ability to bind with organic matter. Soil adsorption coefficient values were calculated by the U.S. Environmental Protection Agency as 1.94 (methylparaben), 2.20 (ethylparaben), 2.46 (propylparaben), and 2.72 (butylparaben)[12], all of which suggest that parabens have the ability to adhere to the organic portion of sediment and sludge, and thus, persist environmentally [13].

Chlorinated parabens are removed from WWTPs with only 40% efficiency in comparison to 92-98% efficiency of parent parabens [2]. The decrease in removal efficiency can be attributed to the decreased biodegradability of chlorinated parabens, their increased overall stability throughout WWTPs, and their relatively low sorption to the sludge phase due to low log Kow values[2].

Higher levels of PHBA are found in tertiary effluent in comparison to paraben derivatives, and PHBA exists in the highest concentration in sewage sludge. There are two reasons for these levels of accumulation. The first reason is PHBA’s tendency to sorb to solid particles, which can be approximated by benzoic acid’s high Kd value of approximately 19. The pKa of PHBA is 2.7, but it is in an environment of a pH between 6-9 [9] [14]. Since the pKa is less than the pH, the carboxylic acid will be deprotonated. The Carboxylate allows it to act as a sorbent on solid environmental matrices, thus promoting its aggregation in tertiary effluent, but especially sewage sludge, which acts as the solid matrix itself. The second reason is due to the intermediate increase in levels of PHBA during the secondary clarifier phase of the WWTP through biological processes.

Environmental concerns with paraben degradation products[edit]

Multiple studies have linked chlorinated parabens to endocrine disrupting functions, specifically mimicking the effects of Estrogen, and chlorinated parabens are believed to be 3-4 times more toxic than their parent paraben[15][16]. In Daphnia magna, general toxicity conferred by chlorinated parabens occurs through non-specific disruption of cell membrane function[16]. The potency of the chlorinated parabens correlates with the propensity of the compound to accumulate in cell membranes [16]. Thus, chlorinated parabens generally increase in toxicity as their ester chains increase in length due to their increased hydrophobicity[16].

The implications of PHBA’s environmental accumulation also warrants attention. If the tertiary effluent is re-used for community use as Greywater, it poses as a hazard to humans. These hazards include, but are not limited to, abnormal fetal development, endocrine disrupting activity, and improper estrogen-promoting effects[17]. If the tertiary effluent is released to the environment in rivers and streams or if the sludge is used as fertilizer, it poses as a hazard to environmental organisms. It is especially toxic to those organisms on lower trophic levels, particularly various algal species. In fact, it has been shown that the LC 50 for a specific algal species, Selenastrum capricornutum, is 0.032 micrograms/L[18]. This is less than the natural abundance of PHBA in tertiary effluent at a level of 0.045 μg/L, thus indicating that current levels of PHBA in tertiary effluent can potentially eradicate more than 50% of Selenastrum capricornutum it comes in contact with.

Removal of parabens through ozonation[edit]

Ozonation is an advanced treatment technique that has been considered as a possible method to limit the amount of parabens, chlorinated parabens, and PHBA that are accumulating in the environment[2].Ozone is an extremely powerful oxidant that oxidizes parabens and makes them easier to remove once subsequently passed through a filter[19]. Due to the electrophilic nature of ozone, it can easily react with the aromatic paraben ring to form hydroxylated products [19]. Ozonation is generally regarded as a less dangerous method of disinfection than chlorination, though ozonation requires more cost considerations [19]. Ozonation has demonstrated great efficacy in the removal of parabens (98.8-100%) and a slightly lower efficacy of 92.4 % for PHBA [2]. A moderately lower rate of removal, however, is observed for chlorinated parabens (59.2%-82.8%)[2]. A proposed reaction mechanism for the removal of parabens by ozonation is detailed mechanistically[19].

Arrow pushing mechanism of the ozonation of parabens.

References[edit]

  1. ^ Yazar K., Johnsson S., Lind M. L., Boman A., Lidén, C. (2011). Preservatives and fragrances in selected consumer-available cosmetics and detergents. Contact Dermatitis. 64: 265–272.
  2. ^ a b c d e f g h i Li W., Shi Y., Gao L., Liu J., Cai Y. (2015). Occurrence, fate and risk assessment of parabens and their chlorinated derivatives in an advanced wastewater treatment plant. Journal of Hazardous Materials 300: 29-38.
  3. ^ a b Wang W., Kannan K. (2016). Fate of Parabens and their Metabolites in two wastewater treatment plants in New York, United States. Environmental science & technology. 50: 1174-1181
  4. ^ Haman C., Dauchy X., Rosin C., Munoz J. (2015). Occurrence, fate, and behavior of parabens in aquatic environments: A review. Water Research. 68: 1-11.
  5. ^ a b c d e f Mao Q., Ji F., Wang W., Wang Q., Hu Z., Yuan S. (2016) Chlorination of parabens: reaction kinetics and transformation product identification. Environ. Sci. Polut. Res. 23, 23081-23091.
  6. ^ a b c d Terasaki M., Takemura Y., Makino M. (2012). Paraben-chlorinated derivatives are found in river water. Environ Chem Lett 10: 401-406
  7. ^ Cherney D. P., Durik S. E., Tarr J. C., Collette T. W. (2006) Monitoring the speciation of aqueous free chlorine from pH 1 to 12 with Raman spectroscopy to determine the identity of the potent low-pH oxidant. Appl. Spectrosc. 60(7), 764-772.
  8. ^ a b Gowda B. T., Mary M. C. (2001) Kinetics and mechanism of chlorination of phenol and substituted phenols by sodium hypochlorite in aqueous alkaline medium. Indian Journal of Chemistry. 40, 1196-1202.
  9. ^ a b Harashit M. (2014) Influence of Wastewater PH on Turbidity. International Journal of Environmental Research and Development. 4, 105-114.
  10. ^ 4-HYDROXYBENZOIC ACID https://pubchem.ncbi.nlm.nih.gov/compound/4-hydroxybenzoic_acid#section=Color (accessed Nov 27, 2017).
  11. ^ Nelly V., Francois L., Loredana V., Maryse D., Louisette L., Jean-Guy B., Rejean B., Francois S., Richard V. (2001) Hydrolysis of 4-Hydrobenzoic Acid Esters (Parabens) and Their Aerobic Transformation into Phenol by the Resistant Enterobacter cloacae Strain EM. Applied and Environmental Microbiology. 67, 2404-2409.
  12. ^ Ferreira A. M., Möder M., Laespada M. E. (2011) Stir bar sorptive extraction of parabens, triclosan and methyl triclosan from soil, sediment and sludge with in situ derivatization and determination by gas chromatography-mass spectrometry. J. Chromatogr. 1218, 3837−3844.
  13. ^ Chunyang L., Sunggyu L., Hyo-Bang M., Yamashita N., Kannan K. (2013) Parabens in Sediment and Sewage Sludge from the United States, Japan, and Korea: Spatial Distribution and Temporal Trends. Environmental Science & Technology. 47(19):10895-10902.
  14. ^ Emmanuel A., Esi A., Lawrence D., Richard A., Gabriel O. (2013) Water quality assessment of wastewater treatment plant in a Ghanaian Beverage Industry. International Journal of Water Resources and Environmental Engineering. 5, 272-279.
  15. ^ Vo T. T. B., Jeung E. B. (2009) An Evaluation of Estrogenic Activity of Parabens Using Uterine Calbindin-D9k Gene in an Immature Rat Model. Toxicological Sciences. 112, 68-77.
  16. ^ a b c d Terasaki M., Makino M., Tatarazako N. (2009) Acute toxicity of parabens and their chlorinated by-products with Daphnia magna and Vibrio fischeri bioassays. J. Appl. Toxicol. 29, 242-247.
  17. ^ Soni M., Carabin I., Burdock G. (2005) Safety assessment of esters of p-hydroxybenzoic acid (parabens). Food and Chemical Toxicology. 43, 985-1015.
  18. ^ 4-HYDROXYBENZOIC ACID. SIDS Initial Assessment Report for 9th SIAM, UNEP, 1999, France.
  19. ^ a b c d Tay K. S., Rahman N. A., Abas M. R. B. (2010) Ozonation of parabens in aqueous solutions: kinetics and mechanism of degradation. Chemosphere. 81, 1446-1453.
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