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Article
Iron-mediated oxidation of methoxyhydroquinone under dark conditions: kinetic and mechanistic insights Xiu Yuan, James A. Davis, and Peter S. Nico Environ. Sci. Technol., Just Accepted Manuscript • DOI: 10.1021/acs.est.5b03939 • Publication Date (Web): 20 Jan 2016 Downloaded from http://pubs.acs.org on January 26, 2016
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Iron-mediated oxidation of methoxyhydroquinone under dark conditions: kinetic and
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mechanistic insights
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Xiu Yuan, James A. Davis, Peter S. Nico
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Earth Sciences Division, Lawrence Berkeley National Laboratory,
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1 Cyclotron Road, Berkeley, CA 94720, United States
6 7 8 9
Resubmitted
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Environmental Science & Technology
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January, 2016
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* Corresponding author. Tel.: +1 (510) 486-7118, Fax: +1 (510) 486-5686
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Email:
[email protected] 18
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ABSTRACT
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Despite the biogeochemical significance of the interactions between natural organic matter
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(NOM) and iron species, considerable uncertainty still remains as to the exact processes
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contributing to the rates and extents of complexation and redox reactions between these
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important and complex environmental components. Investigations on the reactivity of low-
24
molecular-weight quinones, which are believed to be key redox active compounds within
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NOM, towards iron species, could provide considerable insight into the kinetics and
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mechanisms of reactions involving NOM and iron. In this study, the oxidation of 2-
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methoxyhydroquinone (MH2Q) by ferric iron (Fe(III)) under dark conditions in the absence
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and presence of oxygen was investigated within a pH range of 4 – 6. While Fe(III) was
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capable of stoichiometrically oxidizing MH2Q under anaerobic conditions, catalytic oxidation
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of MH2Q was observed in the presence of O2 due to further cycling between oxygen,
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semiquinone radicals, and iron species. A detailed kinetic model was developed to describe
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the predominant mechanisms, which indicated that both the undissociated and mono-
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dissociated anions of MH2Q were kinetically active species towards Fe(III) reduction, with
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the mono-dissociated anion being the key species accounting for the pH dependence of the
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oxidation. The generated radical intermediates, namely semiquinone and superoxide, are of
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great importance in reaction chain propagation. The kinetic model may provide critical
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insight into the underlying mechanisms of the thermodynamic and kinetic characteristics of
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metal-organic interactions and assist in understanding and predicting factors controlling iron
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and organic matter transformation and bioavailability in aquatic systems.
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1. INTRODUCTION
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Natural organic matter (NOM), a chemically diverse mixture of heterogeneous organic
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compounds with various structural and functional properties, is ubiquitous in terrestrial and
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aquatic environments. Considerable attention has been drawn to the redox properties of NOM
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because of its great significance in a wide range of biogeochemical processes including iron
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bioreduction and contaminant transformation. The electron accepting and donating capacities
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of NOM have been attributed to the presence of redox-active constituents, such as quinone
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and phenolic functional groups.1-4 Numerous studies also suggested that quinone moieties in
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NOM not only contribute to the reduction of organic contaminants, such as alkyl halides and
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nitroaromatics, but also stimulate the reduction of ferric oxides by iron reducing bacteria.3-9
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The term quinone collectively refers to organic structures in three oxidation states with one
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electron reduction of a quinone forming a semiquinone radical that can be further reduced to
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the hydroquinone form.10 These species are common constituents of many biologically
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relevant molecules and serve as a vital link in the movement of electrons through cells and
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tissues.8, 11-13 For example, oxidations of dihydroxybenzenes to benzoquinones and
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corresponding back reactions are often reversible under neutral and acidic conditions, earning
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them a prominent place in organic electron transfer chemistry. Further, the frequently
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observed positive correlation between free radical concentrations in NOM and Fe(III)
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reduction using electron spin resonance (ESR) spectroscopy has been attributed to the
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existence of semiquinone radicals, a radical formed either from one-electron oxidation of
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hydroquinones, or from one-electron reduction of quinones, or from one-electron transfer
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from hydroquinones to quinones (a process termed comproportionation).1, 3, 13-15 Though
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commonly presented in very low concentrations due to its high reactivity, semiquinone 3 ACS Paragon Plus Environment
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radicals are kinetically important in the reversible redox chemistry of quinones.9 Previous
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studies also indicated that quinone moieties are important electron-transfer groups in humic
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substances (HS) for both biotic/abiotic reduction and oxidation of HS.1, 16 Besides, recent
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studies by Garg, et al.17, 18 reported that the occurrence of Fe(III) reduction by Suwanee River
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Fulvic Acid (SRFA, a proxy for terrestrial NOM), in non-irradiated acidic solutions was
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mainly attributed to the reduced hydroquinone-like moieties intrinsically presented in SRFA.2,
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4
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important implications and may provide critical information regarding reaction mechanisms
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and functional groups that participate in the mobilization/immobilization of a variety of
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redox-sensitive metals in terrestrial and aquatic environments. For example, hydroquinone
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mediated reduction of Fe(III) could increase the solubility and bioavailability of this critical
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trace element,6 while quinone mediated oxidation of uranium (IV) could affect its mobility
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and thus the remediation of contaminated sites.5
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Iron, as a micronutrient in both aquatic and terrestrial ecosystems, is essential for virtually all
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life forms and plays a critical role in many biogeochemical processes. In natural waters, iron
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exists in two oxidation states, Fe(II) and Fe(III). Despite being more thermodynamically
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stable, Fe(III) quickly hydrolyzes and precipitates at circumneutral pH and thus becomes
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unavailable for direct biological uptake,19 while the reduced form, Fe(II), is much more
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soluble and thus potentially more abundant in a bioavailable form.17 However, in oxygenated
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waters, Fe(II) is rapidly oxidized to Fe(III) at circumneutral pH, which in turn limits its
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bioavailability. Despite the biogeochemical functioning of the equilibration/cycling of
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Fe(II)/Fe(III) couple, fundamental insights into the control and dynamics of interconversion
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between Fe(II) and Fe(III) in natural waters are strictly limited and how these processes
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restrict or enhance iron bioavailability are still largely unknown.
Therefore, studies involving the redox behaviour of quinones in metal reduction have
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Quinones and iron likely coexist in the majority of the natural ecosystem, ranging from the
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surface water to groundwater, from soils to sediments. Since the highly complex nature of
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NOM could potentially interfere with efforts to explore the reactivity of quinone moieties on
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a molecular level, investigations of low-molecular-weight quinones could provide
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considerable insight into the thermodynamics, kinetics, and mechanisms of reactions
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involving quinone moieties.20 Though there is a range of different quinone moieties presented
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in NOM, including benzoquinone-based compounds, such as sorgoleone, and
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naphthoquinone-based compounds, such as juglone and lawsone, as well as anthraquinone-
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based compounds,20 a number of previous studies have indicated that those compounds are
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kinetically closely related to their redox potentials and functional groups, with kinetic
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understanding of one providing a window to interpretation of associated chemistry and
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biochemistry of the other.8, 11, 14, 20-22 2-Methoxyhydroquinone (MH2Q, see abbreviations of
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different quinone species and detailed structure information in Fig.S1 of the Supporting
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Information), as an intermediate product during lignin degradation, is a common constituent
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of NOM and has the highest oxidoreductase activity among a series of low-molecular-weight
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quinones.23, 24 This study therefore investigated the oxidation of MH2Q by Fe(III) under both
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anaerobic and aerobic conditions over the pH range 4 – 6, with emphasis on development of a
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rigorous kinetic description of the oxidation mechanism and insights on the role of free
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radicals, such as semiquinone and superoxide. Thermodynamic characteristics of this system
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were also discussed by employing the half-cell reduction potentials of different redox couples
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to verify modeled rate constants of the reactions involving quinone species. Acidic conditions
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were employed in this study partially to avoid complications associated with the precipitation
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of iron oxides, but they do reflect conditions of acid mine drainage waters and coastal
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environments with the presence of acid sulfate soils.
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2. MATERIALS AND METHODS
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A complete description of the materials and methods used is presented in Section SI2 of the
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Supporting Information (SI).
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2.1. Reagents
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All solutions were prepared using 18 MΩ.cm ultrapure Milli-Q water (Thermo Fisher
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Scientific). Analytical grade chemicals were purchased from VWR International or Sigma-
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Aldrich (or as otherwise stated) and used without further refinement. Stock solutions were
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refrigerated at 4 °C in the dark when not in use. All studies were performed in 10 mM NaCl
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at a controlled room temperature of 22 ± 0.5°C. Experiments were conducted in darkness
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with the reactor covered in foil for the duration of the reaction. Anaerobic data were collected
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in an anaerobic glove bag (Coy Laboratory Products, Grass Lake, MI) filled with 5% H2 and
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95% N2. It is worth mentioning that all the anaerobic experiments conducted in the glove box
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here were completed within 30 min, during which no interference from H2 was observed.
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However, slow reduction of 2-methoxybenzoquinone (MBQ) stock solution to MH2Q during
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an overnight stay in the chamber (more than 17 hr) was observed, suggesting that interference
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reduction from H2 has to be considered for long-term experiments in the glove box.
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2.2. Experimental Measurement
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Measurement of MBQ: Concentrations of MBQ were determined spectrophotometrically
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using a UV-Vis spectrophotometer (Thermo Fisher Scientific) with ε257 = 1.48 × 104 M−1
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cm−1.
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Fe(II) Determination: Concentrations of total Fe(II) were determined using a modified FZ
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method.17
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H2O2 Determination: Previous studies21, 22 indicated the potential interference from
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hydroquinones on H2O2 detection using the fluorescence method,25 therefore, a
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chemiluminescence-based method (the AE-CL method)26 was employed for H2O2
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measurement in this study.
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2.3. Kinetic Modeling
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The kinetic model was fitted to the experimental data over a range of experimental conditions
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using the program Kintek Explorer.27 The sensitivity of the model to changes in individual
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rate constant values was also assessed by examining the change in the relative difference
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between the experimental data and the kinetic model (defined as the relative residual, r) when
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one rate constant was varied while holding the others fixed at their optimal values. The
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program Kintecus28 was employed to evaluate the kinetic model using a VBA program to
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calculate r (see detailed description and Fig.S3 in SI3).
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3. RESULTS AND DISCUSSION
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3.1 Anaerobic Oxidation of MH2Q by Fe(III)
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Previous studies have investigated the redox chemistry of hydroquinones and metal species in
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oxic environments,17, 18, 21, 22, 29 but interaction involving these active components under dark
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anaerobic conditions is also of great interest, not only because such matrix composition better
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features the redox circumstances in anoxic environments (groundwater, deep ocean,
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sediments, et al.), but also the absence of O2 allows full expression of the redox functions of
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metals and quinones and thus enables a thorough estimation of the generation of semiquinone
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radicals under dark anaerobic conditions. Further, the reaction mechanism under anaerobic
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condition is an essential component for the complete kinetic description of the oxidation
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mechanism occurring in the presence of O2. Therefore, in this study, the oxidation of MH2Q
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by Fe(III) was firstly investigated under anaerobic conditions, with results shown in Figures 1
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– 2 (and Fig.S4 and S5). Precipitation of Fe(III) species in the system can be characterized as
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insignificant in these experiments for several reasons: 1) the acidic conditions which enable
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the existence of more soluble Fe(III) species, 2) the very low concentrations of Fe(III)
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employed here, and 3) evidence that > 90% of added Fe(III) was quickly reduced to Fe(II) by
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MH2Q before any significant nucleation/precipitation occurred (Figures 2, 4, and Fig.S8, also
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see detailed explanation in section SI4). Therefore, no further consideration was given to
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precipitation of Fe(III) in this study. Also, Fe(III) and Fe(II) were used as single entities to
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represent all ferric and ferrous species respectively.
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Figure 1 illustrates results for anaerobic oxidation of 500 nM MH2Q by different
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concentrations of Fe(III) at pH 5. The steady-state concentrations of generated MBQ were
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proportional to added [Fe(III)]0, with a specific ratio of 1:2. This is in accordance with
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previous studies30-32 reporting the overall stoichiometry for the oxidation of hydroquinone by
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Fe(III) is: +
( − H ), kanaerobic MH 2 Q + 2Fe(III) → MBQ + 2Fe(II)
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(1)
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which could be further confirmed by Fe(II) generation profiles shown in Fig.S6. At pH 5,
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while 500 nM Fe(III) was completely reduced to Fe(II) at t = 20 min, only ~250nM of MBQ
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was generated. pH dependence of MH2Q oxidation by Fe(III) was shown in Figure 2, as well
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as in Fig.S4 and S5 of the SI. The generation rate of Fe(II), as can be seen from Figure 2,
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increased significantly with increasing pH. For example, in the presence of 500 nM [MH2Q]0,
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500 nM Fe(III) was completely reduced to Fe(II) within 5 min at pH 6, while less than 50%
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of Fe(III) was reduced within the same period at pH 4. Similar trends could also be observed
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in the generation rate of MBQ in Fig.S4 which showed that 250 nM [Fe(III)]0 was capable of
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oxidizing ~120 nM MH2Q in the first 2 min at pH 6 but less than 20 nM MH2Q was oxidized
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in the same duration at pH 4 (Fig.S4, and similar behaviour in Fig.S5). The pH dependence of
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redox reactions between hydroquinones and ferric or cupric species has been previously
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observed and was interpreted in terms of reactions via different ionized forms of
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hydroquinones in various reaction routes.21, 22, 33-37 While the mono-dissociated hydroquinone
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was postulated as the most kinetically active species towards the reduction of metal species,8,
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21, 38
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could also contribute to the reduction of cytochrome c by hydroquinone at acidic pH, which
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is consistent with the conclusion from a recent study on copper-catalyzed oxidation of
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naphthohydroquinone.22
studies by Rich and Bendall35, 36 reported that the undissociated hydroquinone species
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3.2 Aerobic Oxidation of MH2Q by Fe(III)
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The autoxidation of MH2Q (autoxidation is oxidation in the absence of metal catalysts, see
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results in section SI6) was found to be negligibly slow under the conditions of this study,
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principally because of the lower pHs employed here and the high redox potential/pKa's
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possessed by MH2Q,8, 22 making the first electron transfer from MH2Q to O2 highly
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endergonic,4 thus this reaction was not further considered in this study. Fe(III)-mediated
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oxidation of MH2Q in the presence of O2 was inspected, with emphasis on the effects of pH,
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[Fe(III)]0 and [MH2Q]0, as shown in Figure 3. First and foremost, unlike the results obtained
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under anaerobic conditions, non-stoichiometric oxidation, or in other words, catalytic
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oxidation of MH2Q by Fe(III) was observed, especially in Figure 3(D), which demonstrated
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that at pH 6, 500 nM Fe(III) was capable of completely oxidising 10 µM MH2Q within 2 hr.
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Similar tests were also conducted on 1,4-benzohydroquinone and no significant catalytic
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oxidation was found, presumably because the methoxy group substitution lowers the redox
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potential of the hydroquinone and makes it more facile for oxidation by Fe(III).8 Since we
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already confirmed that direct oxidation of MH2Q by O2 is negligible in this system, the rapid
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oxidation of additional MH2Q must occur, at least partially, with mediation of iron.
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It is also noteworthy that Figure 3 showed that Fe(III) oxidizes MH2Q to MBQ in a biphasic
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manner, with initial rapid formation of MBQ followed by a much slower increase in MBQ
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concentration over time. The initial concentration of MBQ that was rapidly formed was
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approximately linear-proportional to the added Fe(III) concentration (similar to anaerobic
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oxidation, where stoichiometric amount of MH2Q was quickly oxidized by added Fe(III)),
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and thus was ascribed to direct oxidation of MH2Q by added Fe(III). This could be further
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justified by Figure 4 and Fig.S8 showing Fe(III) was nearly completely reduced to Fe(II) by
216
the end of the initial rapid phase of oxidation, indicating the direct oxidation of MH2Q by
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Fe(III) is rapid and not rate limiting. Instead, the following much slower process, involving
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multiple O2-mediated reactions, such as regeneration of Fe(III) by oxidizing Fe(II) at such
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acidic pH,39, 40 might be more rate-determining in the overall oxidation.
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On the other hand, it is interesting to notice that in Figure 3, the rate of oxidation is not only
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correlated with the Fe(III) concentration, but also increased with increasing the initial
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concentration of the hydroquinone ([MH2Q]0, Fig.S9), similar to behaviour observed in a
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previous study on copper-mediated oxidation of naphthohydroquinone.22 More specifically,
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as shown in Figure 3(D), at pH 6, more MH2Q was oxidized per unit of time when [MH2Q]0
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= 10 µM than that with [MH2Q]0 = 5 µM; and similarly, comparison between Figures 3(A)-
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(C) and Figure 3(D) indicates that at each pH with [Fe(III)]0 =500 nM, much more MH2Q
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was oxidized per unit of time when [MH2Q]0 = 5 µM than that with [MH2Q]0 = 500 nM. This
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was especially observed within the second oxidation phase, indicating that iron-mediated
229
reactions might not be the only factor dominating the “slow oxidation phase”, and instead
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MH2Q-involved processes must also play a role. Nevertheless, as we declared that the direct
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interaction between MH2Q and Fe(III) is rapid and thus not likely to be rate limiting, other
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reactions involving intermediates generated from MH2Q-dependent activities, most likely the
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semiquinone radicals,21, 22 might be more important in determining the slow oxidation rate.
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Similar to anaerobic oxidation, there is also apparent pH dependence of the aerobic oxidation
235
of MH2Q by Fe(III) (as shown in Figure 3 and Fig.S7 in the SI), i.e., the overall oxidation
236
rate increased with increasing pH from 4 to 6, and such dependence was observed in both
237
oxidation phases (the initial rapid phase and the later slow phase). Apparently, the
238
mechanism accounting for the anaerobic pH dependence (involvement of different ionized
239
forms of MH2Q in reactions with ferric species), is inevitably contributing here, but other pH
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sensitive processes, such as the oxidation of Fe(II) by dioxygen and superoxide,19, 39, 40 could
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also impact the overall pH dependence.
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Besides the generation of MBQ, the transformation of iron in the system is also of great
243
interest. Direct measurement of Fe(II) concentrations over a range of conditions was
244
undertaken in order to assist in determining the mechanism and constraining the fitting
245
parameters. The corresponding results are shown in Figure 4 and Fig.S8. Within the pH range
246
4 – 6, all of Fe(III) added to 500 nM MH2Q solution was quickly reduced to Fe(II), with the
247
reduction rate increasing with increase in pH. As for pH 4 (Fig.S8), the concentration of Fe(II)
248
reached its maximum level after more than 30 min of the reaction initiation, while at pH 6,
249
the highest concentration was quickly achieved within 7 min (Figure 4). Though the re-
250
oxidation of Fe(II) to Fe(III) was happening concurrently,19, 39, 40 this reaction was too slow to
251
compete against the rapid reduction of Fe(III) to Fe(II) by MH2Q. This is to say, all of the
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Fe(III) regenerated from the oxidation of Fe(II) by O2 and other oxidants (such as superoxide
253
and semiquinone radicals, see detailed mechanism in next section and in Table 1) was
254
immediately re-reduced to Fe(II) by MH2Q, thus almost all of the iron was observed as Fe(II)
255
in the system in spite of the predominating oxygenated conditions. The cycling between
256
Fe(III) and Fe(II) kept proceeding until MH2Q was totally consumed, and subsequently the
257
concentration of Fe(II) started to decline simply because of the oxygenation of Fe(II) to
258
Fe(III). This is clearly the case demonstrated in Figure 4 with the top curve representing the
259
reduction of 500 nM Fe(III) by 500 nM MH2Q at pH 6. After the pseudo-equilibrium
260
between Fe(II) and Fe(III) (8 – 60 min), the obvious decrease of [Fe(II)] began at ~ t = 60
261
min, at which point the added 500 nM of MH2Q was nearly completely transformed to MBQ
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(Figure 3(C)).
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In order to gain some insight into the Fe(III)/Fe(II) transformation in the system, the cycling
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rate and the turnover frequency of iron have been calculated using a modified version of the
265
kinetic model reported in Table 1, with detailed description and results provided in Section
266
SI7 (Fig.S12 and S13). As an example, for the case of 500 nM Fe(III) and 10 µM MH2Q at
267
pH 6, cycling between Fe(III) and Fe(II) occurs at the very beginning of the reaction, with a
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turnover frequency of ~6 h−1. By examining the contribution of different oxidants on the
269
oxidation of MH2Q (Fig. S13), it is clear that besides Fe(III)/Fe(II), the O2/O2•− couple, which
270
oxidized almost 40% of MH2Q, is another significant force driving the overall oxidation. This
271
also explains the occurrence of non-stoichiometric oxidation of MH2Q by Fe(III) in the
272
presence of O2. The additional MH2Q was oxidized not only by the regenerated Fe(III) that
273
resulted from oxidation of Fe(II), but also by direct reaction with O2•−, generated either from
274
reduction of O2 by semiquinone or by Fe(II) (reactions 6 and 8, respectively, Table 1).
275
Previous studies also suggested that during the metal-catalyzed oxidation of hydroquinones,
276
stoichiometric amounts of hydrogen peroxide (H2O2) would be generated.8, 22, 41-44 H2O2 is of
277
particular interest because of its ubiquitousness both in the cells of organisms as a by-product
278
of oxygen metabolism, and in surface seawaters primarily due to photochemical processes
279
mediated by NOM.45 A recent study by Murphy, et al.46 also reported rapid production of
280
H2O2 (with maximum concentrations of 3.85 µM) when anoxic groundwater mixed with
281
oxidized, iron rich sediments, indicating a metal redox cycling mechanism under dark
282
conditions. More importantly, in the presence of iron, H2O2 may lead to the formation of
283
highly reactive and damaging oxidants such as hydroxyl radical (HO•), a radical which
284
always present in vanishingly small concentration but will in turn induce the oxidation of
285
both NOM and anthropogenic contaminants.46-48 Therefore the generation of H2O2 during the
286
oxidation of MH2Q by Fe(III) at different pH values was also investigated, with results
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shown in Figure 5. Apparently, the rate of H2O2 generation, similar to the oxidation of MH2Q,
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also exhibited strong pH dependence, with more rapid H2O2 generated at pH 6 than at pH 4.
289
3.3 Kinetic Modelling of MH2Q Oxidation by Fe(III)
290
Since the dissociation states of a hydroquinone is of key importance for its electron-donating
291
capability, the protonation/deprotonation reactions of MH2Q were included in the model as
292
reactions 1 and 2 in Table 1, with previously reported ionization constants.20, 49 Under
293
anaerobic conditions, the oxidation of MH2Q by Fe(III) occurs via direct interactions between
294
Fe(III) and hydroquinone species, and both the undissociated and mono-dissociated
295
hydroquinones have been reported to be active towards reduction of ferric species, as
296
expressed by reactions 3 and 4 in Table 1.34, 36 Although the doubly dissociated species MQ2–
297
is thermodynamically more reactive, its reaction with Fe(III) is negligible in this study
298
considering its extremely low concentration (10–16 – 10–20 M, from pH 6 to 4 under
299
conditions of this study), and thus was not included in the model. The intermediate generated
300
from one electron oxidation of the hydroquinone, semiquinone radical, has been widely
301
proposed to be inevitably involved in the pool with both oxidizing and reducing capibilities.8,
302
18, 21, 34-37
303
included in the model as reaction 5, as well as the oxidation of Fe(II) by MSQ•− (back
304
reaction of reactions 3 and 4) with a reported rate of 1 × 105 M−1·s−1 in recent studies by Garg,
305
et al.17, 18, 29 on iron redox transformations in the presence of natural organic matter.
306
When O2 is present, in addition to those reactions occurring anaerobically, reactions
307
describing the electron transfers between oxygen and semiquinone radical, between
308
superoxide and quinone species, as well as reactions depicting the oxidation of Fe(II), must
309
also be included. The additional reactions included in the model due to the presence of O2
Therefore, the reduction of Fe(III) by 2-methoxysemiquinone radical (MSQ•−) was
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with corresponding rate constants are listed as reactions 6 – 9 in Table 1. As previously stated,
311
the autoxidation of MH2Q is negligibly slow under conditions of this study, and thus was not
312
required in the model. Because O2 has no charge, Marcus theory of electron transfer predicts
313
that rate constants for reaction of semiquinone radical with O2 will be a function of change in
314
the Gibbs free energy.8, 15 It has also been reported that for quinones with a standard mid-
315
point potential of E0(Quinone/Semiquinone) ≥ − 150 mV, rate constants for the forward
316
reactions follow well the Marcus theory for electron transfer and can be estimated by a
317
reported linear relationship.8, 36, 50 Based on this and E0(MBQ/MSQ•−) = − 0.017 V (see
318
detailed calculations in SI8), the rate constant for the forward reaction can be estimated as k6
319
= 1.5 × 106 M−1·s−1. The equilibrium constant (K) of reaction 6 can also be determined by the
320
standard reduction potential (E0) of both redox couples (MBQ/MSQ•− and O2/O2•−) using the
321
Nernst equation:55
322
0 E(O
- E0
-(MBQ/MSQ ) 2 /O 2 )
=
RT ln K nF
(2)
323
where R is the gas constant in appropriate units, 8.314 J K−1 mol−1. T is the temperature in
324
Kelvin, F is the Faraday constant 9.6485 × 104 C mol−1 and n is the number of electrons
325
involved in the reaction. Thus, when n = 1, at 25 °C, Equation (4) can be written as:
326
log K =
0 E(O
- E0
-(MBQ/MSQ ) 2 /O 2 )
(3)
0.059
327
Here we employed the values of E0(O2/O2•−) = − 0.155 V56-58 and E0(MBQ/MSQ•−) = − 0.017
328
V in equation (3) to calculate K6 = 4.58 × 10−3, thus k−6 = k6/K6 = 3.3 × 108 M−1·s−1. These
329
values agree very well with previous reported rate constants of methyl-hydroquinone (k6 =
330
1.2 × 106 M−1·s−1 and k−6 = 7.3 × 108 M−1·s−1),50 which has close redox potentials to MH2Q.
331
Further, because of the substituent effect, the redox potential of MH2Q lies between that of
332
1,4-benzohydroquinone and 1,4-naphthohydroquinone, both the forward and reverse rate 15 ACS Paragon Plus Environment
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333
constants of reaction 6 are also between these two analogous aromatics,21, 22 which again
334
confirms that the redox potential of the quinone/semiquinone couple governs the reaction of
335
semiquinone with dioxygen to form superoxide.8
336
The comproportionation reaction between MH2Q and MBQ was not important in the system,
337
as a result of the extremely low concentrations of the doubly dissociated hydroquinone
338
species (MQ2−, the well-established dominant active species towards comproportionation
339
reaction,15, 34, 36, 49 having a concentration of ~10–16 – 10–20 M from pH 6 to 4 under
340
conditions of this study). Since MSQ•− can be both oxidizing and reducing, it will readily
341
disproportionate to corresponding hydroquinone and quinone. However, due to its low
342
concentration and its rapid removal by dioxygen and iron species (reactions 3 – 6, Table 1),
343
the disproportionation of MSQ•− plays no significant role here. This could be further verified
344
by the result that inclusion of these two reactions in the kinetic model with varying rate
345
constants from 10 – 1010 M−1·s−1 has no observable effect on the overall model fitting
346
(Fig.S3(G) and (H) in SI). Therefore, these two reactions were not included in the model.
347
The oxidation of MH2Q by superoxide, which was expected to have a relatively low reaction
348
rate,58 was included in the model as reaction 7. Previous studies58-60 also suggested that
349
reactions involving H2O2 in this system (such as the backward reaction of reaction 7, Table 1)
350
were not important, presumably because the reaction rate between H2O2 and semiquinones
351
(~104 − 105 M−1·s−1) is low.61, 62 Therefore, this reaction is unlikely to compete effectively
352
with the rapid removal of semiquinones by dioxygen (reaction 6, Table 1). Further evidence
353
for this was given by the sensitivity analysis, which demonstrated that inclusion of this
354
reaction in the kinetic model and varying the rate constant from 10 – 105 M−1·s−1 had
355
negligible effect on the model fitting (see Fig. S3(I) in SI). As such, this reaction was
356
excluded from the model. The disproportionation of O2•−, with rates of 6 × 106 and 6 × 108 16 ACS Paragon Plus Environment
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357
M−1·s−1 at pH 6 and 4 respectively,63, 64 was not important here because of its low
358
concentration and rapid reaction with iron and quinone species (reactions 6 – 9 in Table 1).
359
This was also confirmed by the sensitivity analysis (see Fig.S3(J) in SI). Cross-dismutation
360
between MSQ•− and O2•− might also occur, but little information on this reaction has been
361
previously reported and the rate constant is not known. Inclusion of this reaction in
362
simulations and varying the rate constant over a reasonable range revealed minimal effect on
363
the fitting (Fig. S3(K) in SI), justifying exclusion of this reaction from the model. The
364
oxidation of Fe(II) (reactions 8 and 9), as the key route for regeneration of Fe(III) in the
365
presence of O2, has been extensively investigated at acidic and circumneutral pHs. Therefore,
366
here we employed the well-established pH-dependent rates from previous studies19, 39, 40, 52-54
367
for interactions between O2, Fe(II)/Fe(III) and O2•−.
368
Due to the limited information available in the literature, rate constants for the interactions of
369
Fe(III) and quinone species (reactions 3, 4 and 5, Table 1) and the reaction between MH2Q
370
and O2•− (reaction 7, Table 1) were determined empirically by best fit of the model to the
371
experimental data. Results of model fitting over the pH range 4 – 6 using reactions 1 – 9
372
(Table 1) are illustrated in Figures 1 – 5 (and Fig.S4-S9 in the SI). In general, the model
373
provides reasonable fits to the experimental data over a range of conditions. The good
374
agreement between the model output and the experimental data validates our assumptions of
375
the proposed mechanism and the assignment of individual rate constants.
376
In accordance with previous studies,34-36 both the undissociated and singly dissociated MH2Q
377
species (MH2Q0 and MHQ−) were found to be kinetically active towards Fe(III) reduction
378
with intrinsic rate constants of 2.4 × 103 and 3.0 × 108 M−1·s−1, respectively. Since the
379
standard one-electron reduction potential of the MSQ•−/MH2Q0 couple is much higher than
380
that of the MSQ•−/MHQ− couple (see detailed calculations in SI8), reaction 3 is less 17 ACS Paragon Plus Environment
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381
favourable in a thermodynamic sense and occurs via a rather slower rate than that of reaction
382
4. This again confirms that the mono-dissociated hydroquinone anion is a substantially more
383
facile electron donor to ferric species.8, 34, 36 Although MHQ− only occupies a small fraction
384
of the total hydroquinone species at acidic pH, the protonation/deprotonation equilibrium is
385
faster than that of redox reactions and thus is not rate-limiting.35, 65 It is also worth
386
mentioning that, although thermodynamically less favourable, reaction 3 is still feasible. We
387
can conclude here that the back reaction is more rapid than the forward reaction, since the
388
rate of reaction between Fe(II) and semiquinone radical is almost two orders of magnitude
389
higher than that of the forward reaction. Moreover, the rapid removal of the product, MSQ•−,
390
by Fe(III) and O2 (reactions 5 and 6, respectively) is another significant force driving the
391
oxidation reaction to the right.8, 35 Thus, the presence of O2 in the system not only promotes
392
Fe(III) re-supply by continuously oxidizing Fe(II), but also induces the rapid removal of
393
MSQ•− with resultant generation of O2•−. The model also indicates that the rate of MSQ•−
394
removal by O2 > rate of removal by Fe(III) > rate of removal by Fe(II) > rate of removal by
395
disproportionation, consistent with previously reported conclusion.36 However, unlike the
396
study by Uchimiya and Stone,11 there is no back reduction of MBQ by Fe(II) observed in this
397
study, presumably due to the acidic pH and low concentrations of both reactants employed in
398
this study.
399
The model predicted rate of 1.2 × 107 M−1·s−1 for reduction of Fe(III) by MSQ•− (reaction 5,
400
Table 1) is higher than the value of 2 × 106 M−1·s−1 reported by Yamazaki and Ohnishi34 on
401
the reduction of ferricytochrome c by semiquinones, but lower than the value of 2 × 107
402
M−1·s−1 reported in a recent study on the reduction of cupric species by 1,4-semiquinone.21
403
Furthermore, MSQ•−, with a standard one-electron reduction potential of E0(MBQ/MSQ•−) =
404
− 0.017 V, is more reducing than oxidizing. This is to say, in a system with both Fe(III) and
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405
Fe(II) present, instead of shifting back to MH2Q by oxidizing Fe(II), MSQ•− is more likely to
406
transfer to MBQ by reducing Fe(III), consolidating the model predicted k5 > k-3. As indicated
407
in the study by Eyer,58 the oxidation of MH2Q by superoxide, was expected to have a
408
relatively low reaction rate of ~104 – 105 M−1·s−1.66, 67, 68 Our model predicted rate of 7 × 105
409
M−1·s−1 is also close to the value of 2 × 105 M−1·s−1 reported in recent studies by Garg, et al.17
410
on iron redox transformations in the presence of NOM under acid conditions.
411
Despite the capability of the kinetic model in providing a good description of the various
412
reactions between the quinone triad (MBQ, MSQ•− and MH2Q), Fe(III)/Fe(II), and O2 over a
413
range of experimental conditions with a relatively well-constrained set of rate constants, the
414
model is limited by the assumption that the composite terms Fe(II) and Fe(III) adequately
415
represent all inorganic iron in their +2 and +3 oxidation states, respectively. Therefore, care
416
must be taken when interpreting the model results, since the model is condition-specific by
417
default. For example, the presence of complexing organic ligands would influence the
418
reactivity of various iron species and as such the composite “intrinsic” rate constants of
419
various reactions with iron will need to be re-evaluated.
420
3.4 Implication of Findings
421
In this study, we investigated the oxidation of MH2Q by Fe(III) under dark conditions in the
422
absence and presence of oxygen. While Fe(III) was capable of stoichiometrically oxidizing
423
MH2Q under anaerobic conditions, catalytic oxidation of MH2Q was observed in the presence
424
of O2 due to further cycling between iron, oxygen and semiquinone radicals. Based on the
425
experimental observations, a detailed kinetic model was developed to describe the
426
predominant mechanisms operating in this system and to provide insights into the observed
427
pH dependence and the role of generated radical intermediates. Our results also showed that
19 ACS Paragon Plus Environment
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428
the direct oxidation of MH2Q by O2 is spin-restricted and very slow under conditions of this
429
study, but the Fe(III)/Fe(II) couple could overcome such restriction and perform as an
430
electron transfer agent between the hydroquinone and O2 (similar to previous observed
431
behaviours of copper species21, 22), leading to the existence of pseudo-stable but high
432
concentrations of reduced Fe(II) under oxic and dark conditions that could potentially
433
promote the generation of ROS. One particular example in this study is the generation of O2•−
434
and H2O2 from the redox cycling of iron between its +3 and +2 oxidation states in the
435
presence of MH2Q and O2 confirms the essential role of NOM and reduced metals in non-
436
photochemical pathway for ROS formation in natural aquatic environments,69 which, at the
437
same time, are particularly important for the oxidative degradation of NOM itself and any
438
further cascade of radical-promoted reactions with other constituents in natural waters.
439
Though the presence of O2 is imperative for iron cycling and chain propagating to reach
440
catalytic oxidation of MH2Q in this study, in deep ocean/lakes and groundwater, where O2
441
deficiency prevails, other components presented in such anoxic/anaerobic environments
442
could serve to bridge Fe(II) and Fe(III), and thus facilitate iron cycling and further redox of
443
quinones and NOM. For instance, Uchimiya and Stone11 reported the oxidation of Fe(II) by
444
various quinones at circumneutral pH could serve as a vital link in networks of electron
445
transport in suboxic and anoxic environments. Studies also showed chromium(VI) and
446
manganese(III, IV) (hydr)oxides were capable of oxidising Fe(II) under anoxic conditions.70,
447
71
448
communities may also contribute, especially in low pH environments.72 Therefore, the
449
coexistence of quinones and iron could potentially facilitate the redox cycling of both species
450
in allowable environments, and separately or in concert, iron species (both dissolved and
At the same time, the presence of fluctuating redox conditions and (micro)biological
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451
precipitated) and quinones are believed to be pivotal participants in a wide range of
452
environmental redox reactions.
453
Due to the close correlations between kinetic/thermodynamic characteristics of quinone triads
454
and their structures and functional groups, the kinetic model and associated rate constants
455
reported in this study could provide insight into the rate and extent of interactions between
456
other quinone members and metals that have different electrophilicity and redox potentials.
457
On the other hand, while quinone moieties are recognized to dominate the redox properties of
458
NOM, care must be taken when interpreting the results observed in pure quinone solutions to
459
the natural aquatic environment, where the presence of an extended network of complexing
460
organic ligands would influence the reactivity of various iron species and the stability of
461
radicals. For example, similarities and differences in iron redox transformations between a
462
simple quinone and the quinone moieties presented in SRFA were identified in recent studies
463
by Jiang et al.73 and Garg, et al.,18 where increased stability of semiquinone radicals were
464
found in SRFA solution compared to that in pure hydroquinone solution, indicating quinone
465
moieties presented in highly conjugated and substituted environment of NOM will play a
466
much more important role in the rate and extent of metal redox transformations.
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467
4. ACKNOWLEDGEMENTS
468
The work reported here is supported as part of the Sustainable Systems (SS) Scientific Focus
469
Area (SFA) program at LBNL, funded by the U.S. Department of Energy, Office of Science,
470
Office of Biological and Environmental Research, Subsurface Biogeochemical Research
471
Program, under Award Number DE-AC02-05CH11231. The authors gratefully acknowledge
472
the assistance from Dr. Christopher Miller at the University of New South Wales (Australia)
473
for the model sensitivity calculations.
474
ASSOCIATED CONTENT
475
Supporting Information
476
Additional detailed information on experimental methods, manipulative experiments,
477
sensitivity analysis and extra experimental data and calculation. This material is available
478
free of charge via the Internet at http://pubs.acs.org.
479 480 481 482 483
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58. Eyer, P., Effects of superoxide dismutase on the autoxidation of 1,4-hydroquinone. Chem.-Biol. Interact. 1991, 80, (2), 159-176.
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59. Ishii, T.; Fridovich, I., Dual effects of superoxide dismutase on the autoxidation of 1,4-naphthohydroquinone. Free Radical Biol. Med. 1990, 8, (1), 21-24.
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60. Mochizuki, M.; Yamazaki, S.-i.; Kano, K.; Ikeda, T., Kinetic analysis and mechanistic aspects of autoxidation of catechins. Biochimica et Biophysica Acta (BBA) General Subjects 2002, 1569, (1-3), 35-44.
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61. Kalyanaraman, B.; Sealy, R. C.; Sinha, B., An electron spin resonance study of the reduction of peroxides by anthracycline semiquinones. Biochimica et Biophysica Acta (BBA)General Subjects 1984, 799, (3), 270-275.
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62. Zhu, B.-Z.; Zhao, H.-T.; Kalyanaraman, B.; Frei, B., Metal-independent production of hydroxyl radicals by halogenated quinones and hydrogen peroxide: an ESR spin trapping study. Free Radical Biol. Med. 2002, 32, (5), 465-473.
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63. Zafiriou, O. C., Chemistry of superoxide ion-radical (O2-) in seawater. I. pKasw* (HOO) and uncatalyzed dismutation kinetics studied by pulse radiolysis. Mar. Chem. 1990, 30, 31-43.
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64. Yuan, X.; Pham, A. N.; Xing, G.; Rose, A. L.; Waite, T. D., Effects of pH, chloride, and bicarbonate on Cu(I) oxidation kinetics at circumneutral pH. Environ. Sci. Technol. 2012, 46, (3), 1527-1535.
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65. Adams, G.; Michael, B., Pulse radiolysis of benzoquinone and hydroquinone. Semiquinone formation by water elimination from trihydroxy-cyclohexadienyl radicals. Trans. Faraday Soc. 1967, 63, 1171-1180.
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66. Roginsky, V.; Barsukova, T., Kinetics of oxidation of hydroquinones by molecular oxygen. Effect of superoxide dismutase. J. Chem. Soc., Perkin Trans. 2 2000, (7), 1575-1582.
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67. Kitagawa, S.; Fujisawa, H.; Sakurai, H., Scavenging effects of dihydric and polyhydric phenols on superoxide anion radicals, studied by electron-spin-resonance spectrometry. Chem. Pharm. Bull. (Tokyo) 1992, 40, (2), 304-307. 27 ACS Paragon Plus Environment
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Table 1. Modeled reactions and rate constants of MH2Q oxidation by Fe(III)
691
692 693
a
Unless noted otherwise.
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700
Figure Captions
701
Figure 1. Anaerobic oxidation of 500 nM MH2Q by Fe(III) at pH 5, () [Fe(III)]0 = 100 nM,
702
() [Fe(III)]0 = 250 nM, and () [Fe(III)]0 = 500 nM. Error bars (some of which are too
703
small to be visible) are the standard errors from triplicate measurements, and solid lines
704
represent the model fit using reactions 1 – 5 (Table 1).
705
Figure 2. Generation of Fe(II) from anaerobic oxidation of MH2Q by Fe(III) at different pH,
706
[MH2Q]0 = 500 nM, () [Fe(III)]0 = 250 nM at pH 4, () [Fe(III)]0 = 500 nM at pH 4, ()
707
[Fe(III)]0 = 500 nM at pH 5, and () [Fe(III)]0 = 500 nM at pH 6. Error bars (some of which
708
are too small to be visible) are the standard errors from triplicate measurements, and solid
709
lines represent the model fit using reactions 1 – 5 (Table 1).
710
Figure 3. Aerobic oxidation of MH2Q by Fe(III) at different pH. (A) – (C): [MH2Q]0 = 500
711
nM at (A) pH4, (B) pH5 and (C) pH6 with () [Fe(III)]0 = 100 nM, () [Fe(III)]0 = 250 nM
712
and () [Fe(III)]0 = 500 nM; (D): [Fe(III)]0 = 500 nM at (◇) pH 4 with [MH2Q]0 = 5 µM,
713
() pH 5 with [MH2Q]0 = 5 µM, () pH 6 with [MH2Q]0 = 5 µM, and () pH6 with
714
[MH2Q]0 = 10 µM. Error bars (some of which are too small to be visible) are the standard
715
errors from triplicate measurements, and solid lines represent the model fit using reactions 1
716
– 9 (Table 1).
717
Figure 4. Generation of Fe(II) from aerobic oxidation of MH2Q by Fe(III) at pH 6, [MH2Q]0
718
= 500 nM with () [Fe(III)]0 = 100 nM, () [Fe(III)]0 = 250 nM and () [Fe(III)]0 = 500
719
nM. Error bars (some of which are too small to be visible) are the standard errors from
720
triplicate measurements, and solid lines represent the model fit using reactions 1 – 9 (Table 1).
721
Figure 5. Generation of H2O2 from aerobic oxidation of MH2Q by Fe(III) at different pH,
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722
[MH2Q]0 = 500 nM and [Fe(III)]0 = 500 nM at () pH 4, () pH 5 and () pH 6. Error bars
723
(some of which are too small to be visible) are the standard errors from triplicate
724
measurements, and solid lines represent the model fit using reactions 1 – 9 (Table 1).
725
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726
Page 32 of 34
Figure 1
250
[M B Q ], n M
200 150 100 50 0 0
5
10
15
20
25
30
T im e , m in
727 728 729
Figure 2
500
[ F e ( II) ] , n M
400 300 200 100 0 0
730
5
10
15
20
T im e , m in
731 732 733 32 ACS Paragon Plus Environment
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Environmental Science & Technology
Figure 3
500
500
(A )
(B )
400
[M B Q ], n M
[M B Q ], n M
400 300 200 100
300 200 100
0
0 0
30
60
90
120
150
180
0
30
60
90
T im e , m in
500
10000
(C )
300 200 100
180
(D )
6000 4000 2000
0
0 0
30
60
90
120
150
180
0
20
T im e , m in
40
60
Figure 4
500
[ F e ( II) ] , n M
400 300 200 100 0 0
80
T im e , m in
735
737
150
8000
[M B Q ], n M
[M B Q ], n M
400
736
120
T im e , m in
30
60
90
120
150
T im e , m in
738 739 33 ACS Paragon Plus Environment
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100
120
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740
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Figure 5
300
[ H 2 O 2 ], n M
250 200 150 100 50 0 0
10
20
30
40
50
T im e , m in
741 742 743 744 745
Table of Contents Graphic
746
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