谏壁发电厂7号送风机噪声治理

在分析了送风机主要噪声源及频谱、噪声特性的基础上，应用噪声控制理论，设计并实施了噪声控制方案，达到了预期的治理效果。     

特大型双曲线自然通风冷却塔噪声治理

本文以上海吴泾电厂八期1#、2#机组所用特大型双曲线自然通风冷却塔为例,介绍其噪声特性、控制措施及治理效果。     

基于可接受安全间距的单车道交通流模拟模型

交通流微观模拟是采用计算机对交通流进行描述及分析的方法。尤其对于复杂的交通流而言,微观模拟具有明显的优势,然而模拟的准确与否,关键在于模型的建立。笔者即是在研究我国单车道交通流特点的基础上,借鉴车道变换理论,基于驾驶员可接受的交通安全间距,分析安全变换车道的各间距之间的关系,阐述了有超车的单车道交通流模拟模型的建立方法     

The indirect involvement of buses in traffic accident processes

The involvement of buses in accidents usually is assessed implicitly on the basis of the direct involvement of the bus in the collision or in injury production. This paper deals with the scope and forms of indirect involvement of buses (as a sight obstruction, for example). Accidents were selected by identifying the presence of the term ‘bus’ or synonyms in the text parts of complete police reports (testimonies, statements by the persons involved, etc.) available in electronic form, then analysed in detail. Direct or indirect involvement of a bus is found in 3.6% of traffic injury accidents reported by the police in the community studied (direct involvement: 1.4%; indirect involvement: 2.2%). The different forms of indirect involvement are then described, and some possibilities of preventive measures are discussed.     

重庆市主城区典型道路的交通噪声

选取重庆市主城区典型道路,实测了交通噪声昼夜、水平和垂直变化,结果表明：交通噪声昼夜等效A声级高速公路最高,主干道次之,次干道最低,交通噪声随车流量增加而增大,高峰值出现在上午8：00-10：00和17：00-20：00,最小值出现在凌晨4：00;水平方向上,随着距路沿距离的增加,噪声值逐渐减小,道路路沿45m以外可满足《声环境质量标准》（GB3096-2008）要求;垂直方向上,噪声值先增加后逐渐降低。     

道路交通中苯并(a)芘的高效液相色谱快速测定

用超细玻璃纤维滤膜采集杭州市某道路上机动车排放的苯并（ａ）芘,经超声萃取,高速离心后直接进ＨＰＬＣ分析。在选定的色谱条件下,苯并（ａ）芘与其他多环芳烃完全分离,绝对进样量在０．８～０．０２ ｎｇ时线性良好,相关系数为０．９９９７９,最小检出量０．８ ｐｇ,加标回收率８７．５％～９３．８％。     

杭州区域环境噪声监测点位优化探索

在杭州市现有区域环境噪声手工监测点位的基础上,结合地理分布,采用系统聚类法对2012年149个点位的数据样本分类、合并,将149个点位优化到26个,并用T检验法验证数据可靠性。优化前后各城区的点位分布比例相差不大,等效声级绝对误差在1.0 d B(A)内,相对误差不超过±5%。经过2013年和2014年数据验证,确定优化后的点位能体现声环境功能区的代表性。     

机场噪声自动监测系统应用现状与前景展望

随着我国机场建设规模和覆盖范围逐年扩大,机场噪声带来的扰民问题也愈发严重,机场噪声自动监测系统对于机场运营及周边区域声环境管控显得尤为重要。简述了机场噪声自动监测系统的组成架构、核心功能以及国内外机场噪声自动监测系统发展历程与应用现状,针对技术应用中的局限性问题,提出应建立健全法规标准体系、不断推进系统研发领域、形成社群交互联动机制的建议,为机场噪声自动监测系统应用及环境管理提供参考。     

城区天然气配气站噪声的产生及防治

城区天然气配气站噪声超标已成为供气部门亟待解决的难题,文章分析了配气站噪声污染现状,指出噪声产生原因主要为天然气流动,供气量增长使设备超负荷运行等7个方面。分别针对现有配气站和新建、改扩建站场提出降噪措施,指出设备在额定范围内运行、气体流速控制、工艺改造等是噪声控制的重要手段。并对城区天然气配气站噪声治理的进一步研究提出了建议。     

Spatial & temporal variations of PM10 and particle number concentrations in urban air

The size of particles in urban air varies over four orders of magnitude (from 0.001 μm to 10 μm in diameter). In many cities only particle mass concentrations (PM10, i.e. particles <10 μm diameter) is measured. In this paper we analyze how differences in emissions, background concentrations and meteorology affect the temporal and spatial distribution of PM10 and total particle number concentrations (PNC) based on measurements and dispersion modeling in Stockholm, Sweden. PNC at densely trafficked kerbside locations are dominated by ultrafine particles (<0.1 μm diameter) due to vehicle exhaust emissions as verified by high correlation with NOx. But PNC contribute only marginally to PM10, due to the small size of exhaust particles. Instead wear of the road surface is an important factor for the highest PM10 concentrations observed. In Stockholm, road wear increases drastically due to the use of studded tires and traction sand on streets during winter; up to 90% of the locally emitted PM10 may be due to road abrasion. PM10 emissions and concentrations, but not PNC, at kerbside are controlled by road moisture. Annual mean urban background PM10 levels are relatively uniformly distributed over the city, due to the importance of long range transport. For PNC local sources often dominate the concentrations resulting in large temporal and spatial gradients in the concentrations. Despite these differences in the origin of PM10 and PNC, the spatial gradients of annual mean concentrations due to local sources are of equal magnitude due to the common source, namely traffic. Thus, people in different areas experiencing a factor of 2 different annual PM10 exposure due to local sources will also experience a factor of 2 different exposure in terms of PNC. This implies that health impact studies based solely on spatial differences in annual exposure to PM10 may not separate differences in health effects due to ultrafine and coarse particles. On the other hand, health effect assessments based on time series exposure analysis of PM10 and PNC, should be able to observe differences in health effects of ultrafine particles versus coarse particles.