Weschler C J
Telcordia Technologies, Red Bank, NJ 07701, USA.
Indoor Air. 2000 Dec;10(4):269-88. doi: 10.1034/j.1600-0668.2000.010004269.x.
The concentration of indoor ozone depends on a number of factors, including the outdoor ozone concentration, air exchange rates, indoor emission rates, surface removal rates, and reactions between ozone and other chemicals in the air. Outdoor ozone concentrations often display strong diurnal variations, and this adds a dynamic excitation to the transport and chemical mechanisms at play. Hence, indoor ozone concentrations can vary significantly from hour-to-hour, day-to-day, and season-to-season, as well as from room-to-room and structure-to-structure. Under normal conditions, the half-life of ozone indoors is between 7 and 10 min and is determined primarily by surface removal and air exchange. Although reactions between ozone and most other indoor pollutants are thermodynamically favorable, in the majority of cases they are quite slow. Rate constants for reactions of ozone with the more commonly identified indoor pollutants are summarized in this article. They show that only a small fraction of the reactions occur at a rate fast enough to compete with air exchange, assuming typical indoor ozone concentrations. In the case of organic compounds, the "fast" reactions involve compounds with unsaturated carbon-carbon bonds. Although such compounds typically comprise less than 10% of indoor pollutants, their reactions with ozone have the potential to be quite significant as sources of indoor free radicals and multifunctional (-C=O, -COOH, -OH) stable compounds that are often quite odorous. The stable compounds are present as both gas phase and condensed phase species, with the latter contributing to the overall concentration of indoor submicron particles. Indeed, ozone/alkene reactions provide a link between outdoor ozone, outdoor particles and indoor particles. Indoor ozone and the products derived from reactions initiated by indoor ozone are potentially damaging to both human health and materials; more detailed explication of these impacts is an area of active investigation.
室内臭氧浓度取决于多种因素,包括室外臭氧浓度、空气交换率、室内排放率、表面去除率以及臭氧与空气中其他化学物质之间的反应。室外臭氧浓度通常呈现出强烈的日变化,这为正在起作用的传输和化学机制增添了动态激励。因此,室内臭氧浓度可能会在每小时、每天、季节之间以及不同房间和不同建筑结构之间有显著变化。在正常条件下,臭氧在室内的半衰期在7至10分钟之间,主要由表面去除和空气交换决定。尽管臭氧与大多数其他室内污染物之间的反应在热力学上是有利的,但在大多数情况下反应相当缓慢。本文总结了臭氧与更常见的室内污染物反应的速率常数。结果表明,假设室内臭氧浓度为典型值,只有一小部分反应的速率足够快,能够与空气交换竞争。对于有机化合物来说,“快速”反应涉及具有不饱和碳 - 碳键的化合物。尽管这类化合物通常占室内污染物的比例不到10%,但它们与臭氧的反应有可能作为室内自由基和通常气味很大的多功能(-C=O、-COOH、-OH)稳定化合物的来源而相当显著。这些稳定化合物以气相和凝聚相形式存在,后者对室内亚微米颗粒的总浓度有贡献。实际上,臭氧/烯烃反应为室外臭氧、室外颗粒和室内颗粒之间提供了联系。室内臭氧以及由室内臭氧引发的反应所产生的产物可能对人类健康和材料都造成损害;对这些影响的更详细阐释是一个正在积极研究的领域。