Overview of the Second Texas Air Quality Study (TexAQS II) and the Gulf of Mexico Atmospheric Composition and Climate Study (GoMACCS)



[1] The Second Texas Air Quality Study (TexAQS II) was conducted in eastern Texas during 2005 and 2006. This 2-year study included an intensive field campaign, TexAQS 2006/Gulf of Mexico Atmospheric Composition and Climate Study (GoMACCS), conducted in August–October 2006. The results reported in this special journal section are based on observations collected on four aircraft, one research vessel, networks of ground-based air quality and meteorological (surface and radar wind profiler) sites in eastern Texas, a balloon-borne ozonesonde-radiosonde network (part of Intercontinental Transport Experiment Ozonesonde Network Study (IONS-06)), and satellites. This overview paper provides operational and logistical information for those platforms and sites, summarizes the principal findings and conclusions that have thus far been drawn from the results, and directs readers to appropriate papers for the full analysis. Two of these findings deserve particular emphasis. First, despite decreases in actual emissions of highly reactive volatile organic compounds (HRVOC) and some improvements in inventory estimates since the TexAQS 2000 study, the current Houston area emission inventories still underestimate HRVOC emissions by approximately 1 order of magnitude. Second, the background ozone in eastern Texas, which represents the minimum ozone concentration that is likely achievable through only local controls, can approach or exceed the current National Ambient Air Quality Standard of 75 ppbv for an 8-h average. These findings have broad implications for air quality control strategies in eastern Texas.

1. Introduction

[2] The Second Texas Air Quality Study (TexAQS II)/Gulf of Mexico Atmospheric Composition and Climate Study (GoMACCS) is a joint regional air quality and climate change study. The field measurement component of this study was conducted in eastern Texas and over the neighboring Gulf of Mexico beginning in summer 2005 and continuing through early autumn 2006. The goal of this program is to provide a better understanding of the sources and atmospheric processes responsible for the formation and distribution of ozone and aerosols in the atmosphere and the influence that these species have on the radiative forcing of climate regionally and globally, as well as their impact on human health and regional haze. The eastern Texas region includes two of the ten largest urban areas in the United States: the Dallas−Fort Worth Metroplex and Greater Houston. TexAQS II includes TexAQS 2006, an intensive study period during summer and early autumn 2006 when the major mobile platforms (four aircraft and one ship) were deployed. GoMACCS is aimed at improving the simulation of the radiative forcing of climate change by lower atmosphere ozone and aerosols. In addition to clear-sky radiative effects, GoMACCS investigates the influence of aerosols on cloud properties and the role of clouds in chemical transformations. The TexAQS 2006 and GoMACCS field deployments were simultaneous and utilized the same mobile platforms.

[3] The roles of ozone and aerosols in air quality and climate change issues are often considered to be separate, albeit related, issues. However, the distinction between their roles in these two issues is, at least in part, simply a matter of perspective and scale. Many of the chemical and meteorological processes that affect these two atmospheric species are important to both issues. For example, climate change is usually considered from a global viewpoint where intercontinental transport of ozone and aerosols determines their impact. However, intercontinental transport is either the starting point or the end point of regional air quality concerns, since any particular region contributes outflow to and receives inflow from that transport. This interrelationship of air quality and climate change issues was a foundation of the 2004 International Consortium for Atmospheric Research on Transport and Transformation (ICARTT) study [Fehsenfeld et al., 2006]. The TexAQS/GoMACCS intensive in 2006 continues this approach; the instrumentation and deployment of many of the measurement platforms were planned to simultaneously address the issues involved in both air quality and climate change.

[4] The topics addressed in the present study have a long history. There have been several previous studies conducted in the Texas area. To place the current study into perspective, section 2 provides a brief review of related previous research, most notably the TexAQS 2000 study, which was a direct predecessor of the present field campaign.

[5] The goal of this special journal section is to report many of the TexAQS II/GoMACCS results. The “Final Rapid Science Synthesis Report: Findings from the Second Texas Air Quality Study” (http://www.tceq.state.tx.us/assets/public/implementation/air/am/texaqs/rsst_final_report.pdf) presented an early summary of some of the important findings that were judged to be particularly important for air quality control policy decisions. This document will be referenced below as RSS Final Report.

[6] The overall TexAQS II/GoMACCS study has several individual component programs that have their own goals and objectives; these separate components are briefly described in section 3. Section 4 describes the meteorological conditions under which the measurements took place, and section 5 highlights some of the particularly important findings. The TexAQS II Radical and Aerosol Measurement Project (TRAMP) is part of TexAQS II/GoMACCS, but will publish their results in a separate special section in Atmospheric Environment.

2. Review of Previous Research Related to TexAQS II/GoMACCS

[7] Much of the previous research on air quality in the eastern Texas region has been supported through contracts with the Texas Commission on Environmental Quality (TCEQ) and the Texas Environmental Research Consortium (TERC). The results of this contract research are often not available in peer-reviewed publications. In such cases reports to the funding agency are referenced here to provide the interested reader access to this work.

2.1. Observational Studies of Ozone Formation in the Houston Area

[8] High ozone concentrations in Houston depend strongly upon the interaction of synoptic-scale winds and local coastal/sea breeze oscillations [Banta et al., 2005; Nielsen-Gammon et al., 2005a]. Light to moderate synoptic-scale winds that oppose the direction of the bay breeze arising in the late morning or early afternoon are particularly conducive to ozone formation and accumulation [Banta et al., 2005; Ngan and Byun, 2008; Darby, 2005]. The stagnant conditions that arise from the interaction of these two forces allow ozone precursors to accumulate and react during the warmest and sunniest portion of the day. Later in the afternoon, the southerly Gulf breeze can advect the pool of high ozone across the city [Darby, 2005; Banta et al., 2005].

[9] High concentrations of light alkenes such as propene, ethene, 1, 3-butadiene and butenes have been observed in the Houston metropolitan area, and are closely associated with petrochemical industry facilities in eastern Harris County, Galveston County, Chambers County, and Brazoria County [Ryerson et al., 2003; Daum et al., 2003, 2004; Berkowitz et al., 2004, 2005; Kleinman et al., 2002, 2003, 2005; Jobson et al., 2004; Karl et al., 2003; Buzcu and Fraser, 2006; Xie and Berkowitz, 2006, 2007; Kim et al., 2005]. These compounds collectively labeled as highly reactive volatile organic compounds (HRVOC), and they play a major role in forming the highest concentrations of ozone observed in the Houston area [Ryerson et al., 2003; Daum et al., 2003, 2004; Kleinman et al., 2002, 2005; Wert et al., 2003; Czader et al., 2008]. Historical analyses of routinely collected VOC data indicate that these compounds are present in high concentrations on a routine basis in the Houston area [Hafner Main et al., 2001; Estes et al., 2002; Brown and Hafner Main, 2002; Brown et al., 2002; Brown and Hafner, 2003; Kim et al., 2005; Buzcu and Fraser, 2006; Xie and Berkowitz, 2006, 2007]. Consequently, the high HRVOC concentrations observed during the two field study periods in 2000 and 2006 are not anomalously large, and the conclusions drawn from those data should be generally applicable to the Houston area.

[10] Field study results from 2000 indicate that industrial emissions of HRVOC have been underreported in Houston [Ryerson et al., 2003; Wert et al., 2003; Xie and Berkowitz, 2007; Karl et al., 2003]. Results from more recent studies indicate that these emissions are still underreported [Robinson et al., 2008; Mellqvist et al., 2007; Smith and Jarvie, 2008]. Source apportionment studies have been performed for VOC observations using TexAQS 2000 data [Karl et al., 2003; Zhao et al., 2004] and routine VOC measurements [Buzcu and Fraser, 2006; Buzcu-Guven and Fraser, 2008; Xie and Berkowitz, 2006, 2007; Wittig and Allen, 2008; Kim et al., 2005; Hafner Main et al., 2001; Brown and Hafner Main, 2002; Brown and Hafner, 2003]. These studies have verified that the observed HRVOC are strongly associated with industrial emissions, and the studies have identified specific areas from which the highest HRVOC emissions are emanating. The research efforts have not yet been able to precisely quantify the actual emissions occurring on a long-term basis from the underreported sources. Mellqvist et al. [2007] and Robinson et al. [2008] have had some success in measuring emission fluxes from industrial point sources, but their efforts have been limited to small areas and short time frames. Both of these flux studies have verified that industrial point source emissions for the areas studied are underreported at least part of the time, by factors approaching or exceeding an order of magnitude.

[11] Actual emissions from industrial facilities may vary considerably, owing to periodic or sporadic changes in processes, variations in control efficiency, and accidental or planned releases. Mellqvist et al. [2007] found that the ethene emission flux near the Houston Ship Channel varied by a factor of 10 within 30 min, and smaller variations were common from day to day for propene and total alkanes. However, the exact degree of variation of these emissions, and the quantity, composition and locations of sporadic emissions have not been well quantified. They could account for a relatively large portion of the total annual emissions, on the basis of industry-supplied emission reports [Murphy and Allen, 2005; Webster et al., 2007], but since the reported point source inventory is inconsistent with observations, and thus is inadequately quantified, it is difficult to reach a definitive conclusion.

[12] High concentrations of HRVOC are capable of creating high concentrations of ozone. In Houston, ozone forms rapidly and efficiently in plumes of HRVOC and NOx coemitted from industrial sources [Daum et al., 2003, 2004; Wert et al., 2003; Ryerson et al., 2003; Kleinman et al., 2002, 2005]. The highest ozone observed in Houston is almost exclusively associated with industrial emission plumes [Daum et al., 2004; Ryerson et al., 2003; Berkowitz et al., 2004].

[13] When the United States moved from a standard based on relatively high maximum 1-h average concentrations (120 ppbv) to ones based on much lower maximum 8-h average concentrations (80 ppbv in 1997 and 75 ppbv in 2008) it became clear that the ozone transported into an urban area can contribute significantly toward an exceedance. Nielsen-Gammon et al. [2005b] reported that background ozone concentrations in southeast Texas average about 50 ppbv, with higher concentrations observed with flow from the continental United States, and much lower concentrations observed with flow directly from the Gulf of Mexico.

2.2. Photochemical Modeling of Ozone Formation in the Houston Area

[14] Photochemical grid modeling of the Houston area has been challenging owing to the complex coastal wind circulation, the complex petrochemical point emission sources in Harris, Galveston, Chambers, and Brazoria Counties, and the routine challenges associated with modeling a metropolitan area of over five million inhabitants. One of the purposes of the TexAQS 2000 and TexAQS II field studies was to address the uncertainties that affect photochemical grid modeling and its regulatory applications. The insights gleaned from the TexAQS 2000 and subsequent studies have helped resolve some of these uncertainties.

[15] Several studies have endeavored to identify and reduce the uncertainties in the Houston photochemical grid modeling. Foremost among these efforts are the studies that have sought to quantify underreported industrial HRVOC emissions [Ryerson et al., 2003; Wert et al., 2003; Xie and Berkowitz, 2007; Yarwood et al., 2004; Webster et al., 2007; Smith and Jarvie, 2008] and to assess the sensitivities of ozone simulations to the underreporting of these emissions [Byun et al., 2007; Jiang and Fast, 2004; Nam et al., 2006] (see also TCEQ Houston-Galveston-Brazoria online reports: http://www.tceq.state.tx.us/implementation/air/sip/dec2002hgb.html#docs, http://www.tceq.state.tx.us/implementation/air/airmod/docs/hgmcr_tsd.html, http://www.tceq.state.tx.us/implementation/air/sip/dec2004hgb_mcr.html, http://www.tceq.state.tx.us/implementation/air/airmod/data/hgb1.html#docs, http://www.tceq.state.tx.us/implementation/air/airmod/data/hgb2.html, www.tceq.state.tx.us/assets/public/implementation/air/sip/hgb/hgb_sip_2006/06027SIP_proCh2.pdf, and www.tceq.state.tx.us/assets/public/implementation/air/sip/hgb/hgb_sip_2006/06027SIP_proCh3.pdf). Other modeling efforts have tested different chemical mechanisms in Houston's photochemical grid modeling, in order to study the effects of using different mechanisms on ozone model performance and control strategy effectiveness [Byun et al., 2005b; Faraji et al., 2008; Czader et al., 2008]. Modeling sensitivity studies have also been performed to guide selection of model parameters such as vertical mixing schemes, number and depth of model layers, and horizontal grid resolution [Kemball-Cook et al., 2005; Byun et al., 2005b, 2007; Bao et al., 2005]. TCEQ has supported photochemical modeling efforts since 2000; additional reports can be found at http://www.tceq.state.tx.us/implementation/air/airmod/project/pj_report_pm.html and at http://www.tercairquality.org/AQR/Projects/Modeling.

[16] Mesoscale meteorological modeling is used to drive the photochemical grid models, and many studies have been done to examine and reduce the uncertainties in these models as well. One of the most successful efforts sought to improve meteorological simulations of ozone episodes using radar profiler and other upper level wind data to nudge met modeling [Nielsen-Gammon et al., 2007; Zhang et al., 2007; Stuart et al., 2007; Bao et al., 2005; Fast et al., 2006]. Other efforts improved land cover data and land surface modeling [Byun et al., 2005a; Cheng and Byun, 2008; Cheng et al., 2008], and studied the sensitivity of ozone simulations to solar irradiance and photolysis rates [Zamora et al., 2005; Fast et al., 2006; Pour-Biazar et al., 2007; Byun et al., 2007; Koo et al., 2008]. TCEQ has supported mesoscale meteorological modeling efforts by Nielsen-Gammon and others since 2001; 25 reports about mesoscale meteorological modeling in Houston have been provided to TCEQ, and can be found at http://www.tceq.state.tx.us/implementation/air/airmod/project/pj_report_met.html#met02.

3. Components of TexAQS II/GoMACCS

[17] Sections 3.13.6 describe the principal goals and resources contributed by the independent programs that constituted the larger, 2-year TexAQS II/GoMACCS field program. Appendices A and B give more experimental details of the individual platforms and sites. In addition to the research that is described in this special section, the program also included work conducted by other groups. The Air Quality Research program of TERC funded much of this additional work, including the TexAQS II Radical Measurement Project (TRAMP), the Northeast Texas Plume Study (NETPS), the TexAQS II Tetroon Campaign, research flights of the Baylor University Piper Aztec aircraft and the Houston Triangle Experiment. More information can be found at the TERC website: http://www.tercairquality.org/AQR/.

3.1. TexAQS 2006 and Gulf of Mexico Atmospheric Composition and Climate Study (NOAA)

[18] The NOAA WP-3D and Twin Otter Lidar aircraft combined with the Research Vessel Ronald H. Brown and the radar wind profiler network to conduct the combined TexAQS 2006/GoMACCS study. The WP-3D mapped trace gases, aerosols and radiative properties over the eastern Texas region and the Lidar aircraft, mapped the regional distribution of boundary layer ozone, aerosols and mixing layer heights in the same region. The Ronald H. Brown used both in situ and remote atmospheric sensors to examine low-altitude outflow of pollution from eastern Texas and the chemical environment of the Texas Gulf Coast region. The Radar Wind Profiler Network included ten sites that measured vertical profiles of boundary layer winds (see Appendix B), which provided information on regional-scale trajectories and transport of air masses. The science plan that describes the research aims of Texas 2006/GoMACCS can be found at http://esrl.noaa.gov/csd/2006/.

3.2. Ground Site Network (TCEQ, University of Texas, and Texas A&M University)

[19] TCEQ maintains a network of almost 100 ground stations in eastern Texas that measure and archive concentrations of air pollutants and meteorological data (data are available at the TCEQ web monitoring operations web site: http://www.tceq.state.tx.us/compliance/monitoring/air/monops/hourly_data.html). These sites are operated to assess compliance with National Ambient Air Quality Standards, and consequently the measurements are primarily focused on concentrations of ozone, particulate matter, and their precursors. They are located almost exclusively in urban areas where the potential for human exposures to these air pollutants is greatest. For TexAQS II, additional sites were deployed to provide a combination of upper air meteorological information and surface concentrations of air pollutants in rural areas. More details of these specially deployed sites are given in the descriptions of the Radar Wind Profiler Network and the Surface Air Quality Monitoring Network in Appendix B. The goal of these additional sites was to characterize boundary layer meteorology and surface air quality for the assessment of regional air pollutant transport. Finally, Texas A&M University operated a flux tower with measurements of key constituents in Lick Creek Park, just south of College Station, Texas.

3.3. TexAQS 2006/GoMACCS Aerosol-Cloud Study (National Science Foundation and NOAA)

[20] The CIRPAS Twin Otter aircraft was the primary platform for the aerosol-cloud study. The major scientific objectives centered on the relationship between aerosol physical and chemical properties and the microphysical and radiative properties of the clouds. Therefore, this experiment represents a continuing effort to obtain detailed, in situ field data that will aid in understanding the indirect climatic effect of aerosols. In addition, there was focus on understanding the atmospheric evolution of aerosols. Specific scientific questions included: (1) To what extent can a CCN closure be accomplished; that is, how closely can in situ measured CCN behavior of the ambient aerosol be replicated on the basis of measured aerosol size distribution and composition? This question is of special interest in a heavily polluted urban area like Houston. (2) To what extent can theoretical aerosol-cloud activation models predict cloud droplet number concentrations, given measurements of aerosol size and composition? (3) To what extent do measured radiative fluxes above and below cloud agree with those predicted on the basis of atmospheric radiative transfer models? (4) To what extent can evidence of aerosol effects on cloud microphysics, precipitation initiation and cloud radiative properties be observed? (5) How does entrainment influence cloud microphysics? (6) To what extent can large eddy simulation (LES) of cloud fields predict the statistical properties of those measured? (7) Can the sources and character of the organic portion of the Houston aerosol be understood? (8) What processes govern the evolution of aerosols as they are advected from source-rich areas?

3.4. Satellite Data Integration (NASA, NOAA, and TCEQ)

[21] Scientists from a number of NASA and NOAA satellite groups participated in the TexAQS/GoMACCS field mission. The satellite component contributed to flight planning activities and integrated measurement and modeling studies focusing on influences of continental-scale processes on regional air quality within east Texas. Airborne and surface measurements were used to verify chemical and aerosol analyses and to validate satellite observations on local scales. Ensemble trajectories (sampling analyzed chemical and aerosol fields to account for chemical transformation during transport) were used to identify source regions of pollution sampled by the airborne and surface sensors. Satellite measurements were used to constrain the chemical and aerosol analyses, quantify source strengths and verify model predictions on a regional to global scale.

[22] Satellite instruments are currently able to observe several criteria pollutants in the troposphere including ozone (O3), nitrogen dioxide (NO2), carbon monoxide (CO), sulfur dioxide (SO2) and aerosol optical depth (AOD) (Table A8 in Appendix A). Satellites also provide retrievals of atmospheric thermodynamic properties (temperature, moisture, and clouds) as well as surface and top of atmosphere (TOA) radiative fluxes. Polar-orbiting satellites (e.g., Terra, Aqua, Aura, and the National Polar-Orbiting Operational Environmental Satellite, or POES) provide global coverage once per day and offer a unique vantage point for observing intercontinental pollution transport. Geostationary satellites (e.g., Geostationary Operational Environmental Satellite, or GOES) provide coverage over the continental United States once every fifteen minutes and are useful for following continental-scale pollution transport and regional pollution events. Satellite tropospheric trace gas and aerosol retrievals and area-burned estimates provide valuable information for emission modeling. Long-term, space-based observations place airborne measurements obtained during limited duration field experiments within the context of observed interannual variability and trends.

[23] The availability of near-real-time (within 12–24 h) satellite data significantly increased the role of satellite data in flight planning during TexAQS/GoMACCS. High temporal resolution Step and Stare profile retrievals of tropospheric O3 and CO profiles from the Tropospheric Emission Spectrometer (TES) [Beer, 2006] were available for studying boundary layer exchange processes. 500 mb CO retrievals from the Atmospheric Infrared Sounder (AIRS) [McMillan et al., 2005] provided a regional context for interpretation of ground and airborne measurements. The Multiangle Imaging SpectroRadiometer (MISR) [Diner et al., 1998] provided retrievals of AOD and aerosol type. Aerosol attenuated backscatter measurements from the Cloud Aerosol Lidar with Orthogonal Polarization (CALIOP) instrument onboard the Cloud-Aerosol Lidar and Infrared Pathfinder Satellite Observation (CALIPSO) satellite [Winker et al., 2007] were used to identify the altitude and thickness of regional- and continental-scale aerosol plumes. GOES Aerosol/Smoke Product (GASP) AOD [Knapp et al., 2002] and GOES visible imagery [Gurka et al., 2001] characterized transport of aerosol and smoke plumes. GOES Wildfire Automated Biomass Burning Algorithm (WF-ABBA) [Prins et al., 1998] and MODIS [Giglio et al., 2003] fire detections were used to identify biomass burning sources and provide area-burned estimates for wild fire emissions modeling.

[24] The availability of real-time (within 0–3 h) satellite trace gas and aerosol retrievals allowed chemical and aerosol assimilation/forecast systems to be used for flight planning activities during TexAQS/GoMACCS. Total column ozone retrievals from the Ozone Monitoring Instrument (OMI) [Levelt et al., 2006a, 2006b] and AOD retrievals from the Moderate Resolution Imaging Spectroradiometer (MODIS) instruments [Kaufman et al., 1997] provided for real-time chemical and aerosol data assimilation/forecasting activities. The use of satellite, aircraft, and surface measurements, in conjunction with advanced modeling techniques, supports the development of an Air Quality Assessment and Forecasting capabilities under the U.S. Integrated Earth Observation System (http://usgeo.gov/docs/EOCStrategic_Plan.pdf).

3.5. Airborne High Spectral Resolution Lidar Aerosol Investigations (NASA)

[25] During TexAQS/GoMACCS, the NASA Langley Research Center (LaRC) airborne High Spectral Resolution Lidar (HSRL) was deployed on the NASA B200 King Air aircraft to measure profiles of aerosol extinction, backscattering, and depolarization. These measurements were acquired to address several objectives:

[26] 1. Map the vertical and horizontal distributions of aerosols during transport downwind from major sources. The HSRL profiles provided “curtains” showing the aerosol distributions below the aircraft. Since the lidar measurements clearly depict the altitudes of aerosol layers, they were used to indicate the height to which aerosols are injected into the atmosphere, which is important for modeling the long-range transport of aerosols.

[27] 2. Evaluate measurements from the CALIOP sensor on the CALIPSO satellite. HSRL backscatter, extinction, and depolarization profiles were used to evaluate the CALIOP calibration, as well as the level 1 (attenuated backscatter), and level 2 (aerosol backscatter, aerosol extinction) profiles.

[28] 3. Provide profiles of aerosol extinction, backscatter and depolarization and investigate the use of these profiles to identify aerosol type. The aerosol intensive parameters measured by the HSRL (extinction/backscatter ratio, backscatter wavelength dependence, depolarization) provided a means to identify various aerosol types and investigate the vertical and horizontal variability of aerosol types in the TexAQS/GoMACCS study region, and to determine how aerosol optical thickness was distributed among the various aerosol types.

[29] 4. Characterize the behavior and variability of the planetary boundary layer (PBL) height. Lidar systems have been widely used to examine the structure and variability of the PBL top and to derive the entrainment zone depth [e.g., Cohn and Angevine, 2000; Brooks, 2003]. Since the King Air flew at high (∼9 km) altitude exclusively, the lidar measurements featured long, uninterrupted observations of the PBL and entrainment zone.

[30] 5. Assess model simulations of aerosol extinction profiles. The vertical profiles of aerosol extinction and aerosol intensive parameters measured by the HSRL were used to help evaluate the ability of models to reproduce aerosol extinction profiles and optical thickness.

3.6. IONS-06−NASA

[31] In support of TexAQS II, IONS-06 operated 22 sounding stations (Table A9 in Appendix A) to provide consistently located vertical profiles of ozone concentration over Houston and beyond [Thompson et al., 2008]. IONS-06 was strategically configured to align a group of sites along important transport pathways, i.e., Pacific to western U.S. coast, southwest United States and Mexico toward Houston, Gulf coast and Caribbean toward Houston, and Houston toward Huntsville, Alabama−northeastern North America [Cooper et al., 2007]. At Houston, there were two IONS-06 sampling venues during TexAQS 2006. Launches by G. A. Morris et al. (An evaluation of the influence of the morning residual layer on afternoon ozone concentrations in Houston using ozonesonde data, submitted to Atmospheric Environment, 2009) were performed at the University of Houston (29.7°N, 95.4°W) not far from downtown Houston, 17 August to 5 October 2006. Sondes were also launched from the R/V Ronald H. Brown during August along its cruise track; this series continued through 11 September 2006 [Thompson et al., 2008].

4. Meteorological Context of TexAQS II/GoMACCS

[32] The entire period of TexAQS II (1 June 2005 to 18 October 2006) was unusually dry for the state of Texas as a whole. Drought was widespread November 2005 until January 2007. However, Southeast Texas and the coastal portions of Texas was one of the few areas spared the unusual drought conditions. Figure 1 shows drought conditions across Texas at the beginning and end of TexAQS 2006/GoMACCS intensive field activities of 2006. The drought reached its peak during late August and early September 2006, after which rains helped mitigate conditions. While Houston avoided drought conditions, the Dallas–Fort Worth area was remarkably dry. In August 2006, Bush Intercontinental Airport in Houston (IAH) was 0.6°C above normal, with 89% of normal rainfall, while Dallas−Fort Worth International Airport (DFW) was 3.0°C above normal, with only 26% of normal rainfall. September was a more typical month: IAH saw temperatures 0.5°C above normal with 74% of normal rainfall, while DFW saw temperatures 0.1°C above normal with 107% of normal rainfall.

Figure 1.

Drought conditions in Texas on (left) 1 August 2006 and (right) 10 October 2006, as depicted by the U.S. Drought Monitor. The range of colors from white to dark red correspond to no drought, incipient drought, moderate drought, severe drought, extreme drought, and exceptional drought.

[33] Meteorological differences yield differences in air pollution characteristics between TexAQS 2000 and TexAQS II. TexAQS 2000 took place during a period of substantial drought in southeast Texas, and the very end of August and the first few days of September were characterized by unusually high temperatures that culminated in numerous records being broken. By comparison, the TexAQS II/GoMACCS period was close to normal in the Houston area with respect to both temperature and precipitation.

[34] Typically during August and September, the strong southerly winds of midsummer begin to weaken and cold fronts penetrate southward farther and farther into Texas. Behind the cold fronts, northeast winds tend to bring polluted air from the central and eastern United States. The extent of transport from the northeast controls background ozone levels, while enhancement of ozone due to local emissions depends on the lightness of the winds [Nielsen-Gammon et al., 2005a, 2005b]. Mean winds do not tell the whole story; often just a few days can make an ozone season exceptionally bad.

[35] To help characterize the wind conditions during TexAQS 2006/GoMACCS, Figure 2 shows the mean wind conditions for each day during the field intensive, 1 August 2006 through 15 October 2006. Winds are represented as daily mean winds from buoy 42035, located just offshore from Galveston. Each day's wind is represented by its mean westerly (u) and southerly (v) values, so that a vector drawn from the origin to a given symbol depicts the wind speed and direction for that symbol. The winds during the field intensives of TexAQS 2000 and 2006 are compared with all winds from 1998 through 2006, 1 August through 15 October (blue diamonds) and days with an 8-h maximum ozone greater than 85 ppbv are identified.

Figure 2.

Wind conditions during 1 August through 15 October 1998–2006. Each dot represents the 24-h mean wind measured at Buoy 42035, just offshore of Galveston. The westerly (u) and northerly (v) wind components are given along the x and y axes, respectively; a dot in the northeast quadrant, for example, corresponds to a wind blowing from southwest to northeast. Pink squares are winds during TexAQS 2000. Yellow triangles are winds during TexAQS 2006/GoMACCS. Text insets give number of stations in 2006 exceeding an 8-h ozone average of 85 ppb and the maximum value of 8-h ozone average (ppbv). Dates are given for exceedances of over 100 ppbv. The maroon curve indicates the approximate area of winds conducive to high ozone during 1998–2004.

[36] The distribution of winds during the 2006 field intensive broadly matches the climatology, except for a surplus of strong winds from the south (yellow triangles near the top center of Figure 2) and a deficit of strong winds from the east (lack of yellow triangles near the left of Figure 2). The situation less closely resembles that of TexAQS 2000. TexAQS 2006 did not experience any analogs to the strong westerly flow of 30 August 30 to 1 September 2000 (rightmost pink squares), and conversely, TexAQS 2000 experienced almost no light winds from the northeast even though they were common during TexAQS 2006 and in general.

[37] The maroon line in Figure 2 depicts the margins of wind conditions that were favorable for high ozone during TexAQS 2000. Within this line, the only conditions that occurred in both 2000 and 2006 are light winds from the southeast. In 2000, one such day, 25 August, produced very high ozone concentrations. Yet, in 2006, few such days resulted in high ozone. A check of individual days (not shown) indicates that most of these days involved widespread rain or cloudiness in 2006, suppressing what would otherwise be favorable ozone formation conditions.

[38] The highest levels of ozone within the Houston area during TexAQS 2006 occurred on four Thursdays (17 August, 31 August, 7 September, and 14 September) and one Friday (1 September). As suggested by the mean wind on 1 September being almost directly opposite the mean wind on 31 August, there is some evidence that pollutants from 31 August may have recirculated back into parts of Houston on 1 September. The mean wind on 17 August was also sufficiently close to zero that some recirculation may have been possible under the influence of the sea breeze. In general, though, the high-ozone events during 2006 were less directly influenced by the sea breeze than those of 2000.

[39] Although no high-ozone days occurred in both 2000 and 2006 under similar meteorological circumstances, the combined records from 2000 and 2006 together encompass all common wind scenarios for high ozone in the Houston area.

5. Overview of Results

[40] This section presents an overview of the some of the important results of the TexAQS II/GoMACCS field study, including those published in this special journal section, published elsewhere, and emerging in manuscripts that are still in preparation. Some additional results are described that are presently not included in any planned publications, but are discussed here to give a complete overview of the observational programs involved in TexAQS II/GoMACCS.

5.1. Observational Tests of Emission Inventories

[41] Air quality and climate change problems originate from society's increased emissions of air pollutants and their precursors (VOC, NOx, SO2, CO, air toxics) and radiative forcing agents (CO2, CH4, N2O, halocarbons, black carbon, aerosols). Our understanding of these emissions on both regional and global scales is critically limited. The data collected during this field study provide tests of emission inventories, some of which are summarized here.

5.1.1. Emissions of VOC From Petrochemical Facilities in the Houston Area

[42] Two independent techniques were deployed during TexAQS 2006 to quantify fluxes of ethene from industrial sources near Houston, Texas: a laser photoacoustic spectroscopy (LPAS) instrument on board the WP-3D aircraft [de Gouw et al., 2009] and a solar occultation flux (SOF) instrument operated in a mobile laboratory (J. Mellqvist et al., Measurements of industrial emissions of alkenes in Texas using the Solar Occultation Flux method, submitted to Journal of Geophysical Research, 2009). The latter instrument also measured propene and total alkane fluxes. Both instruments repeatedly quantified ethene fluxes from the Mont Belvieu chemical complex to the northeast of Houston, one of the largest emission sources in the Houston area. The results from the LPAS (520 ± 140 kg h−1) during 10 different WP-3D flights agreed well with those from 6 independent measurements by the SOF (440 ± 130 kg h−1). Two considerations can serve to put these fluxes in perspective. First, the 2006 TCEQ point source database estimated the total ethene emissions from Mont Belvieu to be 81 kg h−1, a factor of 5 to 7 lower than the measured fluxes. Similar discrepancies are generally found throughout the industrial facilities in the Houston area; Mellqvist et al. (submitted manuscript, 2009) found that for all measurements during the campaign, the 2006 emission inventory underestimated the measured fluxes by an average factor of 10 for ethene and 11 for propene. Second, Murphy and Allen [2005] investigated the role of large, accidental releases of HRVOC in ozone formation in the HGB area, and identified 763 HRVOC emission events in a 1-year period. More than half of these events released less than 454 kg total HRVOC. Thus, the Mont Belvieu complex routinely emits more ethene each hour than the total HRVOC released in the majority of the individual accidental release events considered by Murphy and Allen [2005]. The emissions from these facilities represent a much larger source of HRVOC and much more substantial contribution to ozone formation than indicated by current emission inventories.

[43] Results from four different observationally based analyses (ethene/NOx emission ratios in plumes from petrochemical facilities, the ambient distribution of ethene concentrations, the ambient distribution of formaldehyde, and long-term auto-GC ethene measurements) all show evidence for a significant decrease in ethene emissions in the Greater Houston area between the TexAQS 2000 and TexAQS II studies [Gilman et al., 2009] (see also RSS Final Report). The weight of evidence from these four analyses indicates that ethene emissions from the petrochemical facilities decreased by about 40(±20)% (i.e., approximately a factor of 1.7) between 2000 and 2006.

[44] A remarkable finding of the TexAQS II study is that the underestimate of emission fluxes of HRVOC from petrochemical facilities established by the TexAQS 2000 study has not yet been fully integrated into inventories developed since that study. The TexAQS 2000 study established that inventories underestimated these emissions by 1–2 orders of magnitude [Ryerson et al., 2003]. In an analysis prepared for the RSS Final Report, John Jolly of TCEQ reported that total HRVOC emissions included in the Harris County Point Source emission inventory for 2000–2004 were fairly steady across those years, with the lowest year (2002, at 3300 tons) being about 83 percent of the highest year (2004, 4000 tons). Mellqvist et al. (submitted manuscript, 2009) show that there have been some recent, relatively small systematic increases in the inventoried HRVOC emissions; the last eight entries in their Table 3 indicate that inventoried ethene and propene emissions from a large majority of the petrochemical facilities in the Houston area increased from 149 and 176 kg h−1, respectively, in 2004 to 277 and 252 kg h−1, respectively, in 2006. Thus, decreases in actual HRVOC emissions and some increases in inventory estimates have improved the accuracy of the emission estimates, but importantly, inventories still underestimate HRVOC emissions by ∼1 order of magnitude.

[45] A chemically diverse set of volatile organic compounds (VOCs) and other gas-phase species was measured in situ aboard the NOAA R/V Ronald H. Brown as the ship sailed throughout the Houston and Galveston Bay area (HGB) [Gilman et al., 2009]. The reactivities of CH4, CO, VOCs and NO2 with the hydroxyl radical, OH, were determined in order to quantify the contributions of these compounds to potential ozone formation. The total OH reactivity was high in HGB, averaging 10 s−1, primarily owing to the impact of industrial emissions. In comparison, during ship-based measurements downwind from New York City and Boston in 2002, the total OH reactivity only very rarely exceeded 10 s−1 [Goldan et al., 2004]. By compensating for the effects of boundary layer mixing, the diurnal profiles of the OH reactivity were used to determine the source signatures and relative magnitudes of biogenic, anthropogenic (urban + industrial), and oxygenated VOCs as a function of the time of day. This analysis demonstrates that the predominant source of formaldehyde to the air masses sampled by the Ronald H. Brown in HGB was from secondary production, with primary emissions playing only a minor role. The secondary formation of oxygenated VOCs in addition to the continued emissions of anthropogenic VOCs served to sustain elevated levels of OH reactivity throughout the time of peak ozone production.

5.1.2. On-Road Mobile Emission Inventories in the Houston Area

[46] Figure 3 compares CO to NOx ratios from ambient measurements collected during the morning rush hour travel peak with those from emission inventories. The data are treated as described by Parrish [2006]. The Dallas and Houston routine ambient data are in excellent agreement with the nationwide AIRS data. The TexAQS 2006 ratio derived from the TRAMP measurements made at the Moody Tower site (B. Lefer, private communication, 2007) agree reasonably well with the routine monitoring data. The ratios in El Paso and San Antonio are significantly higher, which is attributed to the older vehicle fleets found in those urban areas.

Figure 3.

Measured CO to NOx ratios (solid symbols color-coded according to area) in four Texas urban areas during the morning traffic peak (0600 to 0900 local standard time) compared to the ratio from on-road mobile emissions from the HGB emission inventory (open symbols). The black symbols give the average ratio for all stations in the EPA AIRS network from Parrish [2006].

[47] In Figure 3 the Houston area (indicated as HGB) inventory overestimates the CO to NOx emission ratio, and that overestimate becomes worse with time as the inventory does not show a significant temporal decrease. It should be noted that the on-road emissions inventory value for 2000 was calculated with actual data for 2000, whereas the on-road mobile inventories for later years are less certain projections. Parrish [2006] showed that nation-wide the rapid decrease (6.6%/a) in the CO to NOx ratio is partially due to a slower decrease in CO emissions (4.6%/a), which implies a significant increase in NOx emissions (approximately 2%/a). The large inventory overestimate in the ratio in 2006 is attributed to a factor of 2 overestimate in CO emissions, and an underestimate in present NOx emissions. This causes NOx to CO emission ratios in urban areas, which are often dominated by on-road mobile emissions, to be underestimated by current emission inventories.

[48] Urban emission ratios sampled by the WP-3D aircraft in 2006 and the NCAR Electra aircraft in 2000 are consistent with measurements carried out at a Houston highway tunnel in 2000 [McGaughey et al., 2004]. These measurements demonstrate the weekday increase in CO/CO2 and CO/NOx emission ratios from midday to the afternoon rush hour correlated with increases in the proportion of gasoline vehicles during rush hour. Similar to the routine monitors, the aircraft and tunnel observations indicate that inventories overestimate mobile source CO by at least a factor of 2. Comparison of the 2000 and 2006 aircraft data suggests that urban CO emissions declined by roughly a factor of 2 between the studies (using either CO2 or NOx as a comparison) in agreement with the National Emission Inventories from 1999 and 2005, which show a similar decline (G. J. Frost et al., manuscript in preparation, 2009).

5.1.3. Marine Vessel Emissions in the Texas Gulf Coast Region

[49] Gaseous and particulate emissions from commercial marine shipping were investigated through measurements made in more than 200 exhaust plumes from a variety of ships encountered by the Ronald H. Brown throughout the Gulf Coast region of Texas including most of the major ports and the Houston Ship Channel. Gas-phase and particulate emission factors were determined under actual operating conditions and compared with published emission factors used for emission inventory modeling.

[50] E. J. Williams et al. (Emissions of NOx, SO2, CO, H2CO and C2H4 from commercial marine shipping during TexAQS 2006, submitted to Journal of Geophysical Research, 2009) show that bulk freighter and tankers emitted considerably more NO2 per unit fuel burned than do underway container carriers, passenger vessels, or tugs. Emission of SO2 was higher for all cargo vessels than for passenger ships or tugs, which is due to the use of higher sulfur residual fuels by cargo ships and lower sulfur distillate fuels by passenger ships and tugs. There is broad general agreement between these data and published emission factors, although variability is large for both cases. Marine vessel emission factors for NO2 and SO2 are considerably larger than for stationary sources such as coal-fired or gas-fired power plants, which indicates that emissions from commercial marine vessels likely make significant contributions in coastal areas and ports.

[51] Lack et al. [2008] measured particulate emission factors for these same ships, and found the emission of black carbon (BC) from these diesel engine powered vessels was a factor of 2 greater than previous estimates. They found that tugs emit more BC than do large cargo vessels, which has particular significance for the Houston-Galveston region since these vessels constitute a large fraction of total ship traffic there. Lack et al. [2009] also found that the chemical composition (sulfate and organic material) and aerosol properties such as single-scatter albedo and particulate water uptake of ship exhaust particulates was directly related to the fuel sulfur content.

5.1.4. Biogenic Emissions in the Eastern Texas Region

[52] C. Warneke et al. (Biogenic emission measurement and inventories: Determination of biogenic emissions in the eastern United States and Texas and comparison with biogenic emission inventories, submitted to Journal of Geophysical Research, 2009) utilize airborne measurements of isoprene and monoterpenes conducted during the TexAQS 2006 campaign along with results from the SOS 1999, TexAQS 2000, and ICARTT 2004 studies to evaluate the biogenic emission models BEIS3.12, BEIS3.13, MEGAN2 and WM2001. Two methods are used for the evaluation. First, the emissions are directly estimated from the ambient isoprene and monoterpene measurements assuming a well-mixed boundary layer and using calculated OH concentrations, and are compared with the emissions from the inventories extracted along the flight tracks using measured light and temperature. Second, BEIS3.12 is incorporated into the detailed transport model FLEXPART, which allows the isoprene and monoterpene mixing ratios to be calculated and compared to the measurements. The overall agreement for all inventories is within a factor of two and both methods give consistent results. MEGAN2 is in most cases higher, and BEIS3.12 and BEIS3.13 lower than the emissions determined from the measurements. Regions with clear discrepancies are identified. For example, an isoprene hot spot to the northwest of Houston, Texas, is expected from BEIS3 but not observed in the measurements. Interannual differences in emissions were also observed: the isoprene emissions estimated from the measurements in Texas in 2006 may have been 50% lower than in 2000 under the same light and temperature conditions.

5.1.5. Ammonia Emissions in the Eastern Texas Region

[53] Ammonium nitrate aerosol is formed from the reaction of gas-phase ammonia (NH3) and nitric acid (HNO3). High-time-resolution (∼1 s average) NH3 measurements were made from the WP-3D aircraft by a Chemical Ionization Mass Spectrometry technique [Nowak et al., 2007] and from the Ronald H. Brown by quantum cascade laser absorption (S. C. Herndon et al., manuscript in preparation, 2009) with the goals of characterizing sources and examining the effect of NH3 on atmospheric aerosol formation.

[54] Mixing ratios measured aboard the WP-3D aircraft over the Houston urban area ranged from 0.2 to 3 ppbv, and generally decreased with increasing altitude (J. B. Nowak et al., manuscript in preparation, 2009). Though infrequent, plumes with NH3 mixing ratios from 5 to greater than 50 ppbv were observed in the boundary layer below 1 km altitude. Corresponding increases in fine particle volume and particulate nitrate (NO3) and decreases in HNO3 mixing ratios typically accompanied the large observed NH3 enhancements. These correlated variations are consistent with ammonium nitrate formation. NH3 mixing ratios as high as several hundred ppbv were measured in the HSC from the Ronald H. Brown. Up to this point, it has proven difficult to trace the sources of plumes with high NH3 concentrations to particular industrial facilities.

[55] Power plants that have installed Selective Catalytic Reduction (SCR) units constitute a possible NH3 source. This process adds aqueous NH3 to the exhaust gases as a reagent to decrease NOx emissions. NH3 “slippage,” i.e., unwanted emissions of NH3 into the atmosphere, occurs when exhaust gas temperatures are too low for the SCR reaction to proceed to completion, or when excess NH3 is added. The W.A. Parish electric generating facility is equipped with these units, and the WP-3D aircraft sampled the Parish plume on numerous flights during TexAQS 2006. Clear enhancements of CO2, NOy, and SO2 were observed, but no difference in NH3 mixing ratios could be discerned during the plume transect. The lack of NH3 enhancement in the power plant plumes sampled by the WP-3D indicates that NH3 slippage was not significant during any of the TexAQS 2006 plume transects.

5.2. Air Quality: Measurements and Observational Based Analyses

5.2.1. Role of Nitrate Radicals and N2O5

[56] Hydrolysis of N2O5 provides a nonphotochemical mechanism for conversion of NOx to soluble nitrate (NO3) that can be competitive with, or even exceed, photochemical oxidation of NO2 by OH. Formation of N2O5 proceeds through oxidation of NO2 to NO3 by ozone and further reaction of NO3 with NO2. The process is only important in the dark because of the photochemical instability of NO3. Hydrolysis of N2O5 occurs heterogeneously via uptake to aerosol. Its rate therefore depends on the availability of aerosol surface area and on the heterogeneous uptake coefficient of N2O5 to aerosol, γ(N2O5). Both are highly variable, making the dark loss of NOx more difficult to accurately predict than the photochemical loss via OH reaction.

[57] Measurements of NO3 and N2O5 from the NOAA WP-3D aircraft on night flights allowed the direct determination of the overall loss rates for N2O5 and for its heterogeneous uptake coefficient [Brown et al., 2009]. The γ(N2O5) values derived from the field measurements were considerably smaller than predictions from current model parameterizations based on laboratory data. The result is consistent with the one set of previous aircraft determinations of N2O5 heterogeneous hydrolysis rates in the northeast United States [Brown et al., 2006], which showed small γ(N2O5) on mixed organic/neutral ammonium sulfate aerosol. This aerosol type was prevalent during TexAQS 2006. Lifetimes of N2O5 were long enough to allow overnight transport of reactive nitrogen in this form from large NOx emission sources in the Houston area to rural regions of eastern Texas.

5.2.2. Role of Halogen Radicals

[58] The TexAQS-GoMACCS 2006 study provided the first ambient measurements of nitryl chloride, ClNO2 [Osthoff et al., 2008]. This active chlorine species is produced in the reaction of N2O5 with chloride-containing aerosol particles, and was observed at mixing ratios as high as 1.2 ppbv, much higher than models had previously predicted. ClNO2 is photolyzed to form chlorine atoms in the morning hours when other sources of reactive radicals are low, which can “kick start” the ozone formation process, an effect that was demonstrated by a simple box model described by Osthoff et al. [2008]. ClNO2 also acts to preserve NO2 against the loss to particles through N2O5 heterogeneous uptake. This NO2 is then available for photochemical reaction the next morning.

[59] A regional modeling study using the TexAQS-GoMACCS 2006 ClNO2 observations as a starting point [Simon et al., 2009] found only modest (up to 1.5 ppbv) effects on ozone in the HGB area if the ClNO2 is produced only in the surface layer at the coast, i.e., where the measurements were made. The ClNO2 ambient measurements, and subsequent laboratory studies (J. M. Roberts et al., manuscript in preparation, 2009) showed that significant N2O5 to ClNO2 conversion takes place at chloride concentrations as low as 0.05M. In addition, studies of N2O5 uptake on substrates of low pH (<2) show that molecular chlorine can be produced from this reaction directly [Roberts et al., 2008]. Thus, the potential of this chemistry to affect urban photochemistry deserves further study. Although ClNO2 was not measured from the WP-3D aircraft, examination of its potential formation from N2O5 uptake to chloride-containing aerosol aloft showed that halogen activation by this mechanism may have been substantial in some NOx plumes.

5.2.3. Photochemical Ozone Production

[60] The NOAA WP-3D aircraft conducted extensive studies of anthropogenic emissions and the subsequent ozone and reactive nitrogen photochemistry in the continental boundary layer downwind of the Houston, Texas urban area. Measurements of ozone, CO, NOx, and NOx oxidation products were made during 65 crosswind transects of plumes from the greater Houston urban/industrial area performed on 10 daytime under a variety of meteorological conditions [Neuman et al., 2009]. On all days when the CO to NOy enhancement ratios in downwind plume transects were unambiguously interpretable, the ozone production efficiency derived from observed O3 to NOy-NOx enhancement ratios averaged 5.9 ± 1.2 in coalesced plumes from urban and petrochemical industrial sources in Houston. Higher values were observed in isolated plumes downwind from petrochemical facilities located along the Houston ship channel.

5.3. Air Quality: Meteorological and Modeling Studies

5.3.1. Interregional and Long-Range Transport

[61] During the last decade, emission control measures have successfully reduced the highest ozone concentrations observed in the urban areas of Texas as well as elsewhere in the United States [e.g., Environmental Protection Agency, 2004]. During this same period the basis of the ozone standard was changed from a maximum 1-h average to a maximum 8-h average. Both of these changes increased the importance of the background ozone contributions to violations in urban areas. Thus, urban air quality control strategies increasingly depend upon understanding the sources of the background ozone and the mechanisms and magnitude of its interregional and long-range transport into urban areas.

[62] Several studies during TexAQS II focused on the contribution from background ozone transport into the eastern Texas urban areas [Kemball-Cook et al., 2009; Langford et al., 2009; Pierce et al., 2009; R. M. Hardesty et al., manuscript in preparation, 2009; D. W. Sullivan, Regional ozone and particulate matter concentrations during the Second Texas Air Quality Study, submitted to Journal of Geophysical Research, 2009]. These papers define “background ozone” somewhat differently and utilize different approaches to determine that background, but they all present findings consistent with the conclusion that the transport of background ozone can predominate over in situ production within the urban area, even during exceedance conditions. For example, Langford et al. [2009] and Kemball-Cook et al. [2009] report background ozone values spanning the approximate ranges of 15 to 80 ppbv and 22 to 72 ppbv, respectively. Since the ozone standard has recently been lowered to 75 ppbv for an 8-h maximum daily average, it is clear that background ozone alone can bring an area close to the exceedance level.

[63] A regional model [Kemball-Cook et al., 2009] and a global model [Pierce et al., 2009] also provided estimates of background ozone. Both models predict enhanced background ozone concentrations associated with air masses transported into eastern Texas from upwind regions. Both models have some success in reproducing the magnitude and temporal variability of background ozone determined by the experimental based studies, and agree that areas from the entire eastern United States contribute to the eastern Texas background ozone.

5.3.2. Ozone Transport Downwind of Source Regions

[64] C. J. Senff et al. (manuscript in preparation, 2009) analyzed airborne lidar ozone measurements to estimate the horizontal flux of ozone in urban plumes downwind of Houston and Dallas. Aircraft transects across the plumes downwind of the source regions enabled calculation of total ozone in the plume. By combining the measured plume ozone with the local wind speed extrapolated from multiple wind profiler observations, the net flux of ozone into rural areas downwind of the urban centers was computed. Three Houston cases from the 2006 study were compared with similar measurements from TexAQS 2000, as well as with a single 2006 Dallas case. In Houston, highest flux levels were measured for cases when winds were southerly and indicated significant transport of ozone into rural areas north of Houston. The limited data available indicate that the net ozone flux transported out of Houston averaged about a factor of two to three larger than the corresponding flux from Dallas.

5.3.3. Boundary Layer Effects

[65] On the Ronald H. Brown, a Doppler lidar was used to measure mixing heights and profiles of wind speed and turbulence while the ship was in operation [Tucker et al., 2009]. The results were used to investigate the effects of mixing heights and turbulent mixing on shipboard in situ chemistry and aerosol measurements. Observations showed a significant difference in the diurnal cycle of mixing heights for ship locations in or near the Houston Ship Channel, in Galveston Bay, or in the Gulf of Mexico. Additionally, the observations showed the necessity of taking into account mixing layer and turbulence characteristics in the interpretation of the chemical species and aerosol observations. Daytime planetary boundary layer (PBL) heights also were determined from the NASA King Air with the HSRL. Appendix A provides some details of this determination. The mean (std. dev.) PBL height was 1.3 km (0.48 km) while the mean entrainment zone thickness was 200 m (140 m). PBL heights over the Gulf of Mexico were typically several hundred meters lower than the PBL heights over land.

5.3.4. Effect of Local Wind on Peak Ozone Concentration

[66] Ozone concentrations measured by the network of surface stations around Houston and by the airborne ozone lidar were analyzed by R. M. Banta et al. (manuscript in preparation, 2009) to assess the role of local winds on peak ozone concentrations. They found that vector wind speed was inversely proportional to daily peaks in ozone concentrations in the Houston area. Hardesty et al. (manuscript in preparation, 2009) also investigated the correlation between high ozone in the Houston urban plume, as measured by the airborne lidar, and wind speed and found a similar result. In both studies the depth of the mixing layer was shown to have little impact on ozone concentrations investigated.

5.3.5. Ozone and PM2.5 Model Forecasts

[67] McKeen et al. [2009] evaluate seven real-time air quality forecast models (AQFMs) against observations from the AIRNow surface network and NOAA WP-3 aircraft data collected over eastern Texas during the TexAQS 2006 field study. Forecast performance statistics for surface O3 and PM2.5 are presented for each model as well as the model ensemble, and these statistics are compared to previous real-time forecast evaluations during the ICARTT/NEAQS 2004 field study in New England. Surface maximum 8-h daily average O3 forecasts for eastern Texas during the summer of 2006 show a marked improvement in correlations, bias and RMSE-based skill scores for all models compared to similar forecasts for New England during the summer of 2004. Though some of this improvement may be due to the smaller region, and more spatially uniform meteorological forcing during the 2006 study, improvements in all the AQFM formulations and emissions have also occurred since 2004. As found in the 2004 study, the ensemble mean of the model forecasts outperforms any single model. In contrast to the bulk statistical measures only the two Canadian AQFMs were able to forecast the 85 ppbv 8-h average O3 exceedances better than persistence. All other AQFMs as well as the ensemble mean showed far less skill at threshold exceedance predictions compared to New England in 2004. Considering the ensemble mean as the best, most representative realization of the model suite, the number of 85 ppbv O3 exceedances was severely underestimated for the Houston region, but much less so for the Dallas/Fort Worth region. This preferential underprediction for Houston is consistent with low ethene emission biases for Houston.

[68] Statistical evaluations of the PM2.5 forecasts, based on 24-h averages, are much less reliable during TexAQS 2006 compared to ICARTT/NEAQS-2004. All of the models except one are biased low. Correlations and RMSE-based skill for all models, and their ensemble, are much smaller in 2006 compared to 2004 and fall well below persistence. The low biases suggest a missing component to the PM2.5 forecasts. The daytime aircraft comparisons of PM2.5 yield a different picture, similar to aircraft comparisons in 2004, with most models showing positive bias compared to the PM volume measurements. This is despite the fact that all models severely underpredict organic- PM2.5, the dominant component of ambient PM2.5. This discrepancy can be explained by an overestimation of primary, unspeciated PM2.5 emissions within the inventories compensating the lack of secondary organic aerosol formation within the models.

[69] Experience with air quality model forecasts during TexAQS 2006 and in New England in 2004 suggest that there are at least three essential requirements for improving photochemical model forecasts. First, improved emission inventories are required for AQFMs (and as well for diagnostic models); second, an improved understanding of the chemical mechanisms responsible for the formation of secondary organic aerosols must be developed and incorporated into the model chemical mechanisms; and third, sophisticated data assimilation of meteorological and even chemical observations is likely required.

5.4. Aerosol Formation, Composition, and Chemical Processing

5.4.1. In Situ Measurements of Aerosol Composition and Evolution

[70] Aerosols over the Gulf of Mexico during August 2006 were heavily impacted by dust from the Saharan Desert and acidic sulfate and nitrate from ship emissions [Bates et al., 2008]. The mass loadings of this “background” aerosol were much higher than typically observed in the marine atmosphere and substantially impacted the radiative energy balance over the Gulf of Mexico as well as the particulate matter (PM) air quality in the Houston-Galveston area. As this background aerosol moved onshore, local urban and industrial sources added an organic rich submicrometer component. Hydrocarbon-like organic aerosol concentrations and CO mixing ratios were highest in the early morning when the source was strong (automobile traffic) and mixing was limited (shallow, stable boundary layer) and then decreased during the day as the boundary layer mixing height increased [Bates et al., 2008]. Sulfate and oxygenated-organic aerosol concentrations followed the opposite pattern. Concentrations were lowest in the shallow, stable nocturnal boundary layer and increased during the day as the boundary layer mixing height increased, reflecting their secondary source. Secondary organic aerosol (SOA) formation and growth in the urban plumes of Houston and Dallas were similar to plumes sampled downwind of urban areas in NE United States. Higher SOA growth rates were measured downwind of the Houston Ship Channel, most likely a result of the higher VOC mixing ratios [Bahreini et al., 2009]. However, the model predicted amounts of SOA were on average a factor of 2–3 lower than the measurements [Bahreini et al., 2009]. Positive matrix factorization analysis of organic functional groups and trace metals attributed most of the organic carbon in the measured ambient aerosol directly to oil and biomass combustion emissions [Russell et al., 2009].

5.4.2. Remote Sensing of Aerosol Composition

[71] HSRL measurements of aerosol properties acquired during TexAQS/GoMACCS were used to identify aerosol types and apportion aerosol optical thickness to each aerosol type (R. Ferrare et al., Airborne high spectral resolution lidar aerosol measurements during MILAGRO and TexAQS/GoMACCS, paper presented at Ninth Conference on Atmospheric Chemistry, American Meteorological Society, San Antonio, Texas, 2007, available at http://ams.confex.com/ams/pdfpapers/119758.pdf). Aerosol depolarization ratio at 532 nm, backscatter color ratio (backscatter at 532 nm/backscatter at 1064 nm), extinction-to-backscatter ratio (“lidar ratio”), and the spectral dependence of aerosol depolarizations (i.e., (depolarization at 1064)/(depolarization at 532 nm)) were used in a cluster analysis procedure to identify classes of aerosol as defined by observed natural groupings of intensive optical properties. The optical properties of each cluster were then used to infer which aerosol type(s) most closely matched that cluster. The aerosol properties observed during TexAQS were usually characteristic of spherical aerosols associated with biomass burning and/or urban pollution. These urban/biomass type aerosols accounted for about 73% of the aerosol optical thickness measured by the HSRL during TexAQS/GoMACCS. This is in contrast to the Mexico City region during the Megacity Initiative: Local and Global Research Observations (MILAGRO) mission in March 2006, when the aerosol type consisting of a mix of dust and urban aerosols accounted for over half of the aerosol optical thickness (AOT) measured by the HSRL. The aerosol types observed during TexAQS/GoMACCS were also similar to the aerosol types measured by the HSRL over the eastern United States. However, there were a few occasions during TexAQS when nonspherical dust aerosols were observed. In particular, Saharan dust was observed over the Gulf of Mexico southeast of Houston on 28 and 29 August [Liu et al., 2008].

5.4.3. In Situ Measurements of Aerosol Optical and Hygroscopic Properties

[72] Massoli et al. [2009] measured aerosol optical and hygroscopic properties on board the NOAA R/V Ronald H. Brown. Aerosols from fresh traffic emissions had the lowest single scattering albedos (ω) and were the least hygroscopic (lowest γ values). The more aged aerosols had progressively larger values of ω and γ, and sulfate-dominated aerosols exhibited the highest values of ω and γ. D. P. Atkinson et al. (Comparison of in situ and columnar spectral measurements during TexAQS-GoMACCS 2006: Testing parameterizations for estimating aerosol fine mode optical properties, submitted to Journal of Geophysical Research, 2009) measured aerosol extinction on the Moody Tower and used the combined Moody Tower and Ronald H. Brown data sets to identify two periods when the Houston and Galveston areas were affected by large-scale aerosol events, one of which was coarse mode dominated and one fine mode dominated. They then compared the in situ measured fine mode fraction of extinction and fine mode effective radius with that obtained through various AERONET data processing algorithms.

5.5. Aerosol Cloud and Radiative Effects

5.5.1. Aerosols as CCN

[73] Lance et al. [2009] analyzed in situ cloud condensation nuclei (CCN) measurements obtained on the CIRPAS Twin Otter, focusing in detail on a CCN closure study within and downwind of the Houston regional plume and over the Houston Ship Channel. CCN closure was evaluated by comparing measured CCN concentrations with those predicted on the basis of measured aerosol size distributions and Aerosol Mass Spectrometer (AMS) particle composition. Generally, CCN concentrations were overpredicted by 3% to 36%. It is hypothesized that variation in the externally mixed fraction of the aerosol accounts for much of the variability in the CCN closure, while the composition of the internally mixed fraction largely controls the over prediction bias.

[74] Quinn et al. [2008] measured CCN aboard the NOAA R/V Ronald H. Brown and showed that the mass fraction of hydrocarbon-like organic aerosol (HOA) explained 40% of the variance in the critical diameter for particle activation at 0.44% supersaturation. In locations impacted by urban, industrial, and marine vessel emissions, HOA dominated the mass in the sub-200-nm size range.

5.5.2. Aerosol-Cloud Relationships in Continental Shallow Cumulus

[75] CIRPAS Twin Otter measurements in the Houston region were used to study the effect of variations in aerosol concentration on the properties of continental warm cumulus clouds. Fourteen intensive cloud measurement flights included three in which isolated cumulus clouds of sufficient size and lifetime existed to allow detailed sampling; the other 11 cases involved scattered cumuli that yielded statistical properties over the cloud field [Lu et al., 2008]. Cloud droplet number concentration was found to be clearly proportional to the subcloud accumulation mode aerosol number concentration. Cloud liquid water content, cloud droplet number concentration, and cloud top effective radius exhibited subadiabaticity resulting from entrainment mixing processes. The degree of LWC subadiabaticity was found to increase with cloud depth. It is estimated that owing to entrainment mixing, cloud LWP, effective radius, and cloud albedo were decreased by 50–85%, 5–35%, and 2–26%, respectively, relative to adiabatic values of a plane-parallel cloud. The observations are used to develop cloud top LWC and drop effective radius parameterizations that should prove useful for representation of these small cumulus clouds in larger-scale models.

5.5.3. Large Eddy Simulation of Aerosol-Cloud Relationships in Continental Shallow Cumulus and Comparison With Measurements

[76] On the basis of aircraft sampling strategy and availability of data, five research flights of the CIRPAS Twin Otter were deemed most suitable for large eddy simulation (LES) modeling. The LES model was coupled to a bin microphysical model representing warm cloud processes, a radiation model, and a land surface model over a 12.8 km × 12.8 km × 5 km domain (grid size 100 m in the horizontal and 50 m in the vertical). The model was initiated with observed environmental profiles. The simulations generated an ensemble of thousands of cumulus clouds for statistically meaningful comparisons with the observed clouds. Normalized frequency distributions of simulated and observed parameters including liquid water content, drop number concentration, drop effective radius, updraft velocity, and the distribution of cloud sizes, were shown to be in good agreement [X. Jiang et al., 2008]. These comparisons suggest that the LES model is able to successfully simulate both the microphysical and macrophysical properties of the cloud fields observed during GoMACCS.

5.5.4. Effect of Aerosol on Measured and Modeled Three-Dimensional Spectral Irradiance in Broken Cloud Fields

[77] Schmidt et al. [2009] compared measured solar spectral irradiance from broken boundary layer clouds embedded in moderately to heavily polluted air masses with modeled irradiance using three-dimensional radiative transfer applied to the output of large eddy simulation [H. Jiang et al., 2008]. Upwelling and downwelling moderate resolution irradiance spectra from 380 nm to 2150 nm were measured aboard the CIRPAS Twin Otter. The model reproduced the measured irradiance only when interstitial aerosol particles were included in the simulations. The aerosol particles enhanced fractional absorption in the layer by 20% for the case examined in this study. The simulations allowed for the discrimination between true and apparent forcing and the results showed that aerosol particles increased the relative radiative forcing at the surface by as much as 8%. These findings represent an important new mechanism that is not represented in any current assessment of aerosol (either direct or indirect) cloud radiative forcing. In addition, the good comparison between LES-modeled and measured irradiance fields provides confidence that the LES represents not only the microphysical and macrophysical cloud properties described in section 5.5.3, but also their radiative response to aerosol.

6. Conclusions

[78] The measurements collected during TexAQS II and the shorter TexAQS 2006/GoMACCS intensive period provide very useful data sets, which have only been partially examined by the analyses presented in this special journal section, and briefly summarized in this paper. The data are available to the atmospheric chemistry community for further analysis, and future papers are planned that will extend the results presented here. Two present results are worthy of particular emphasis. First, despite decreases in actual HRVOC emissions and some improvements in inventory estimates since the TexAQS 2000 study, the current Houston area emission inventories still underestimate HRVOC emissions by approximately 1 order of magnitude. Second, the background ozone transported into the urban areas of eastern Texas, which represents the minimum ozone concentration that is likely achievable through only local controls, can approach or exceed the current National Ambient Air Quality Standard of 75 ppbv for an 8-h average. These findings have broad implications for air quality strategies in eastern Texas.

Appendix A:: Mobile Platform Instrument Payloads and Deployment Details

[79] The NOAA WP-3D aircraft was instrumented to study aerosol composition and gas-phase chemical transformations. The aircraft operated from the PBL up to 6.5 km and had sufficient range to sample throughout eastern Texas and the Gulf of Mexico while based at Ellington Field in Houston, Texas, from 31 August through 13 October. Tables A1a and A1b summarize the characteristics of the WP-3D instrumentation, and Table A2 and Figure A1 summarize the TexAQS II/GoMACCS flights.

Figure A1.

Flight tracks of the NOAA WP-3D aircraft during TexAQS II/GoMACCS. The heavier black outlines indicate the two major urban areas in the region: Dallas–Fort Worth to the north and Houston to the south.

Table A1a. NOAA WP-3D Aircraft Instrumentation for Gas-Phase Measurements
Species/ParameterReferenceTechniqueTime Resolution, sInaccuracy (1 sigma)Imprecision (1 sigma)
  • a

    Sampling time depends on aircraft altitude.

NORyerson et al. [1999]O3-induced chemiluminescence (CL)15%0.015 ppbv
NO2Ryerson et al. [2000]UV photolysis–CL19%0.040 ppbv
NOyRyerson et al. [1999]Au converter–CL112%0.200 ppbv
O3Ryerson et al. [1998]NO-induced CL13%0.050 ppbv
COHolloway et al. [2000]VUV resonance fluorescence15%0.500 ppbv
CO2Daube et al. [2002]NDIR absorption10.08 ppmv0.110 ppmv
SO2Ryerson et al. [1998]Pulsed UV fluorescence310%0.300 ppbv
C2-C10 NMHCsSchauffler et al. [1999]whole air sample/GC-FID8–30a5–10%0.003 ppbv
C1-C2 halocarbonsSchauffler et al. [1999]whole air sample/GC-MS8–30a2–20%<0.050 ppbv
C1-C5 alkyl nitratesSchauffler et al. [1999]whole air sample/GC-MS8–30a10–20%0.0002 ppbv
isoprene, monoterpenes, CH3CN, oxygenates, and aromaticsde Gouw et al. [2003]Proton transfer reaction mass spectrometry (PTRMS)1710–20%<0.250 ppbv
C2H4de Gouw et al. [2009]laser photoacoutic absorption spectroscopy (LPAS)2010%0.700 ppbv
HCHOWeibring et al. [2007]Difference frequency generation tunable diode laser absorption113%0.220 ppbv
PAN, PPN, PiBN, APAN, MPAN, MoPANSlusher et al. [2004]I chemical ionization mass spectrometry (CIMS)230% (100% for MPAN)0.020 ppbv
NO3, N2O5Dubé et al. [2006]Cavity ring-down spectroscopy (CARDS)120%0.002 ppbv
NH3Nowak et al. [2007]protonated acetone dimer CIMS125%0.080 ppbv
HNO3Neuman et al. [2002]SiF5 CIMS115%0.100 ppbv
HO2 + RO2Eisele and Tanner [1993]NO titration–NO3 CIMS1040%5 × 106 cm−3
H2SO4Eisele and Tanner [1993]NO3 CIMS1030%1 × 106 cm−3
UV-VIS actinic fluxStark et al. [2007]spectrally resolved radiometry using hemispheric collectors in zenith and nadir115% (30% for jO1D) 
Visible and IR irradiancePilewskie et al. [2003]Solar Spectral Flux Radiometer13–5%0.2%
H2O tunable diode laser spectrometry11.0°C0.3°C
H2O chilled mirror hygrometry11.0°C1.0°C
Table A1b. NOAA WP-3D Aircraft Instrumentation for Aerosol Measurements
Species/ParameterReferenceTechniqueTime ResolutionNotes
Aerosol number, size, and volume distributionsBrock et al. [2000, 2003]Wilson et al. [2004]five parallel CPCs, and white and laser light scattering with a low turbulence inlet (LTI)1 s0.004–8.3 μm physical diameter
Black carbonSchwarz et al. [2008]single-particle soot photometry1 smixing state, mass, and optical properties
Cloud condensation nucleiLance et al. [2006]streamwise thermal gradient continuous flow CCN counter1 soperated at multiple supersaturations
Aerosol bulk ionic compositionWeber et al. [2001]Particle into liquid sampling–ion chromatography (PiLS-IC)3 minanion and cation data in submicron range
Aerosol water-soluble organic carbonSullivan et al. [2006]PiLS–total organic carbon detection (PiLS-TOC)15 sin submicron range
Aerosol chemical composition (size-resolved, nonrefractory)Bahreini et al. [2008]Aerosol mass spectrometry (AMS)10 s100% transmission from 0.055 to 0.360 μm physical diameter
Table A2. NOAA WP-3D Flights
Flight NumberFlight DescriptionDate in 2006Takeoff–Landing LST
    1Transit from Tampa to Houston; Beaumont–Port Arthur (BPA) and Houston-Galveston (HGA) plumes31 Aug1115–1530
    2Oil platform emissions and processing in Gulf of Mexico11 Sep1005–1630
    3Houston and Dallas emissions and processing; coordinated with NOAA Twin Otter and NASA King Air13 Sep1045–1645
    4Houston emissions and chemical processing; coordinated with CIRPAS Twin Otter and NASA King Air15 Sep0950–1620
    5Houston emissions; NE Texas power plants and aged Houston plume16 Sep0955–1630
    6Houston urban, Parish power plant, isolated refineries19 Sep0950–1620
    7BPA, Houston urban, Parish power plant, isolated refineries20 Sep0955–1615
    8Houston urban and industrial plumes; Parish power plant21 Sep0950–1625
    9Dallas, GMD tower, Big Brown, and Parish power plants25 Sep0945–1625
    10Houston, Parish power plant, BPA, and Lake Charles, Louisiana plumes26 Sep0950–1635
    11Houston, Parish power plant, Beaumont–Port Arthur27 Sep1245–1755
    12Houston, Parish power plant, chemical processing into the night29 Sep1345–2010
    13Houston, Parish power plant emissions and processing5 Oct0950–1620
    14Houston, Parish power plant, Victoria and Seadrift6 Oct0950–1600
    15Houston, Parish power plant, chemical processing into the night8 Oct1520–2200
    16Oklaunion power plant at night10 Oct1720–2400
    17Houston emissions and processing at night12 Oct1920–0005
    18Transit from Houston to Tampa; Texas and Louisiana emissions13 Oct0945–1530

[80] The NOAA Twin Otter aircraft was flown with a downward-looking lidar to characterize the regional boundary layer structure of ozone and aerosol backscatter (R. J. Alvarez II et al., manuscript in preparation, 2009). Observations were used to identify and track the Houston urban plume, estimate the amount of ozone exported from Houston and Dallas, and investigate the relationship between ozone concentration and boundary layer structure. The aircraft typically flew just above the boundary layer to produce vertical profiles of boundary layer ozone concentration and aerosol backscatter with a horizontal resolution of 600 m and vertical resolutions of 90 m (ozone) and 6 m (aerosol backscatter). To improve precision, the ozone lidar data are reported with a 450-m vertical running average; more details are given by Alvarez et al. (manuscript in preparation, 2009). The Twin Otter was on site in southeast Texas from 1 August to 13 September during which time it obtained roughly 70 h of ozone/aerosol observations over 21 flights. Table A3 and Figure A2 summarize the TexAQS/GoMACCS Twin Otter flights, showing the emphasis on flights around Houston.

Figure A2.

Composite of all NOAA Twin Otter flight tracks for which lidar data are reported during TexAQS 2006. Regions are designated for regional analysis of background ozone.

Table A3. NOAA Twin Otter Flights
Flight NumberFlight DescriptionDate 2006Takeoff–Landing LST
    1Transit from Boulder to Houston with refueling stop in Wichita Falls, Texas; measured ozone south of Dallas and north of Houston1 Aug0815–1600
    2Houston/ship channel plume with clean southerly flow3 Aug1145–1615
    3Houston/ship channel plume with easterly flow; overflight of Ronald H. Brown4 Aug1110–1600
    4Potential stagnation and sea breeze front5 Aug0940–1320
    5Sea surface calibration measurements, Ronald H. Brown overflight8 Aug1330–1740
    6Ship channel plume; significant interference from convection10 Aug1250–1600
    7CALIPSO underflight with Ronald H. Brown; Houston/ship channel plume north of Houston12 Aug1130–1720
    8Houston/ship channel plume with clean southerly flow14 Aug1220–1830
    9High ozone in Houston area, elevated mixed layer depths, sea breeze incursion15 Aug1315–1855
    10Weak ESE winds, high ozone levels in plume N of Houston16 Aug1305–1930
    11High ozone level under northeasterly flow, multilayered aerosol structure S and SW of Houston17 Aug1150–1750
    12Sampling in Dallas area: instrument and convection problems limited data21 Aug0900–1800
    13Instrument test, Ronald H. Brown overflight22 Aug0950–1410
    14Instrument test, Houston heat island, Galveston Bay24 Aug1435–1820
    15Coordinated mission with King Air and CIRPAS Twin Otter, Ronald H. Brown overpass28 Aug1130–1620
    16Ozone plume south of Houston under northerly flow30 Aug1220–1845
    17Houston plume under easterly flow, high-ozone day31 Aug1105–1710
    18Sea breeze recirculation, high ozone1 Sep1310–1820
    19Ozone transport into Texas from the east, high ozone west of Houston4 Sep1055–1505
    20MISR overflight, ozonesonde comparison, measurements upwind and downwind of Houston under easterly flow7 Sep0920–1620
    21Ozone transported into Texas along Texas-Louisiana border8 Sep0910–1510
    22Ozone downwind of Dallas, P-3 and King Air intercomparisons13 Sep1120–1750

[81] The NOAA Research Vessel Ronald H. Brown departed Charleston, South Carolina on 27 July 2006, arriving initially in Galveston, Texas, on 2 August 2006. The cruise track included passages into Port Arthur/Beaumont, Matagorda Bay, Freeport Harbor, Galveston Bay to Barbours Cut (15 transits), and the Houston Ship Channel (4 transits). The cruise ended in Galveston, Texas, on 11 September 2006. Approximately 50% of the sampling time was spent in the Gulf of Mexico and 50% within the interior waters of Texas. The cruise tracks are shown in Figure 1 of Bates et al. [2008]. The ship was instrumented to measure an extensive set of in situ gas and aerosol parameters as well as many remotely sensed parameters (Table A4). Radiosondes (2–8 times per day) and ozonesondes (once per day) also were launched from the ship.

Table A4. NOAA Research Vessel Ronald H. Brown Instrumentation
Species/ParameterReferenceTechniqueAveraging TimeDetection LimitUncertainty
JNO2 Photolysis ratesShetter et al. [2003]Filter radiometer1 min4.0 × 10−6 Hz±12%
JNO3 Photolysis ratesStark et al. [2007]Filter radiometer1 min1.3 × 10−5 Hz±14%
JO3(1D) Photolysis ratesBohn et al. [2004]Filter radiometer1 min1.1 × 10−7 Hz±26%
OzoneBates et al. [2005]UV absorbance1 min1.0 ppbv±1.0 ppbv or 2%
OzoneWilliams et al. [2006]NO chemiluminescence1 min0.1 ppbv±2%
Ozone vertical profilesThompson et al. [2000]Ozonesondes1 s (= 5 m)2 ppbv3–5%
Ozone vertical profilesZhao et al. [1993]O3 lidar (OPAL)10 min5 ppb<10 ppb
Carbon monoxideGerbig et al. [1999]UV fluorescence1 min1.5 ppbv±3.0%
Carbon dioxideLiCor specNondispersive IR1 min<1 ppmv0.08 ppmv
Water vaporCalculatedRH/temperature probe1 min0.1 ppthv±5%
Sulfur dioxideBates et al. [2005]Pulsed fluorescence1 min0.1 ppbv<±5%
Nitric oxideFehsenfeld et al. [1990]Chemiluminescence1 min0.010 ppbv±(3.8% + 0.010 ppbv)
Nitrogen dioxideRyerson et al. [2000]Photolysis cell1 min0.060 ppbv±(13% + 0.093 ppbv) @ NO2/NO = 3
Total nitrogen oxidesWilliams et al. [1998]Au tube reduction1 min0.08 ppbv±(15% + 0.08 ppbv)
PANsSlusher et al. [2004]TD/CIMS1 minPAN/PPN (2 pptv); tPBN/APAN (4 pptv)PAN/PPN ± (2pptv + 15%) tPBN/MPAN ±(4 pptv + 20%)
Alkyl nitrates, hydrocarbonsGoldan et al. [2004]GC/FID/MS5 min≤1 pptv±20%
Continuous speciation of VOCsWarneke et al. [2005]PIT-MS/CIMS1 min0.05–0.50 ppbv20%
NO3/N2O5Dubé et al. [2006]Cavity ring-down spectroscopy1 s1 pptv1 pptv, ±30%
NO2Osthoff et al. [2006]Cavity ring-down spectroscopy1 s0.20 ppbv0.20 ppbv, ±8%
HNO3/soluble NO2/soluble ClDibb et al. [2004]Automated mist chamber/IC5 min5 pptv15%
HCHO/HCOOHHerndon et al. [2007]TILDAS1 s0.180 ppbv10%
HO2/RO2Green et al. [2006]PERCA1 min2 pptv40%
HgSholupov et al. [2004]Atomic absorption spect.1 s<5 ng m−3±(1.5–2.6) ng m−3
RadonWhittlestone and Zahorowski [1998]Radon gas decay13 min  
Seawater and atmospheric pCO2Sabine et al. [2000]Nondispersive IR30 min ±0.2 ppm
Seawater DMSBates et al. [2000]S chemiluminesence30 min0.2 nM±8%
Aerosol ionic compositionBates et al. [2008]PILS-IC5 min0.1 μg m−3±20%
Aerosol WSOCBates et al. [2008]PILS-TOC1 min0.1 μg m−3±17%
Aerosol size and compositionBates et al. [2008]Q-AMS5 min0.1 μg m−3±20%
Aerosol size and compositionDeCarlo et al. [2006]HR–TOF-AMS1–10 s0.05 μg m−3±20%
Aerosol OCBates et al. [2008]Online thermal/optical45 min0.1 μg m−3±21%
Aerosol organic functional groupsGilardoni et al. [2007]FTIR spectroscopy of <1 μm particles on Teflon filters4–12 h1 μg±15%
Aerosol organic speciationThornberry et al. [2009]Collection/thermal desorption/PTR-MS10 min0.02 μg m−3 
Aerosol composition, 2 stage (sub/super micron) and 7 stage at 60% RHBates et al. [2008]Impactors (IC, XRF and thermal optical OC/EC, total gravimetric weight)4–12 h ±6–31%
Total and submicron aerosol scattering and backscattering (450, 550, 700 nm) at 60% RHQuinn and Bates [2005]TSI 3563 nephelometers (2)1 min ±14%
Total and submicron aerosol light scattering hygroscopic growthCarrico et al. [2003]Twin TSI 3563 nephelometers RR M903 nephelometer20 s (over each 1% RH)σspTSI: 1.85 and 2.78 σbsp: 1.24 and 2.96 σspRR: 1.06σspTSI: −14 ∼ 17 σbsp: −17 ∼ 19
Total and submicron aerosol absorption (450, 550, 700 nm) drySierau et al. [2006]Radiance Research PSAPs (2)1 min ±22%
Submicrometer aerosol absorption (532 nm) dryLack et al. [2006]Photoacoustic Aerosol Absorption Spectrometer1 min0.1 M m−1±5%
Total and submicron aerosol extinctionBaynard et al. [2007]Cavity ring-down spectroscopy1 min0.01 M m−1±1%
Total and submicron aerosol light extinction hygroscopic growthMassoli et al. [2009]Cavity ring-down spectroscopy1 min0.01 M m−1±5%
Aerosol numberBates et al. [2001]CNC (TSI 3010, 3025)1 s ±10%
Aerosol size distributionBates et al. [2005]DMA and APS5 min ±10%
Cloud condensation nucleiQuinn et al. [2008]DMT CCN counter30 min ±10%
Aerosol optical depthQuinn and Bates [2005]Microtopsintermittent ±0.015 AOD
Aerosol backscatter vertical profilesZhao et al. [1993]O3 lidar (OPAL)10 min1 * 10−6 m−1 sr−130% aerosol backscatter
BL wind/aerosol/turbulenceGrund et al. [2001]Doppler lidar (HRDL)0.5 s2–6 km10–12 cm s−1
Wind/temperature profilesLaw et al. [2002]915-MHz wind profiler5 min0.5–5 km±1.4 m s−1
Temperature/RH profilesWolfe et al. [2007]Sondes5 s0.1–18 km±0.3°C ±4%
Radiative fluxesPilewskie et al. [2003]Spectroradiometers1 Hz 3–5%
Cloud heightFairall et al. [1997]Ceilometer15 s0.1–7.5 km±30 m
Cloud drop size, updraft velocityKollias et al. [2001]3-mm Doppler radar5 s0.2–12 km-
Turbulent fluxesFairall et al. [2003, 2006]Bow-mounted EC flux package20 Hz 10 min, 1 h2 W m−2 0.002 N m−2±25% at 1 h
Low-altitude temperature profilesCimini et al. [2003]60-GHz scanning microwave radiometer10 s0–0.5 km±0.3°C
Wind profiles/microturbulence below cloudFrisch et al. [1989]Comstock et al. [2005]C band radar5 min0.1–2 km±1.0 m s−1

[82] The CIRPAS Twin Otter Aircraft was based at Ellington Field in Houston, Texas, during August–September 2006. The aircraft payload consisted of a wide array of instrumentation for aerosol and cloud physical, chemical, and radiative characterization (Table A5). The general focus of the mission was on characterizing aerosol and cloud properties, from within the boundary layer up to the free troposphere. A variety of air mass types was sampled during this study, including plumes from coal-fired power plants, air over and downwind of the Houston Ship Channel, and air over the Gulf of Mexico. Table A6 lists the research flights during GoMACCS, and Figure A3 shows the individual flight tracks.

Figure A3.

Flight paths of the CIRPAS Twin Otter flights during GoMACCS. These are the 10 flights that intercepted clouds most appropriate for study.

Table A5. CIRPAS Twin Otter Aircraft Instrumentation for Aerosol and Ancillary Data Measurements
ParameterReferenceTechniqueAveraging TimeDetection LimitSize Range Detected
Particle number concentrationMertes et al. [1995] and Buzorius [2001]condensation particle counter (TSI CPC 3010)1 s0–10,000 particles/cm3Dp > 10 nm
Cloud condensation nuclei concentrationRoberts and Nenes [2005]Lance et al. [2006]continuous flow streamwise thermal gradient CCN counter (DMT)1 s0–10,000 particles/cm3N/A
Aerosol size distributions at dry and humid conditionWang and Flagan [1990] and Wang et al. [2003]scanning differential mobility analyzer (dual automated classified aerosol detector (DACAD))73 sN/A10–700 nm
Aerosol size distribution passive cavity aerosol spectrometer (PCASP)1 sN/A0.1–2.6 μm
Aerosol bulk ionic composition and soluble organic compositionWeber et al. [2001] and Sorooshian et al. [2006]particle-into-liquid sampler (PILS)5 m0.02 – 0.28 μg/m3 (depending on species)<1 μm
Aerosol bulk composition (nonrefractory species)Jayne et al. [2000] and Bahreini et al. [2003]Aerodyne quadrupole aerosol mass spectrometer (AMS)30 s or 1 m0.02 – 2.3 μg/m3 (depending on species)Dva ∼ 40 nm to 1 μm
Soot absorptionArnott et al. [1999, 2006]photoacoustic absorption spectrometer1 s1 M m−110 nm to 5 μm
Soot absorptionBond et al. [1999]particle soot absorption photometer (PSAP)1 s or higherN/AN/A
Soot absorptionBaumgardner et al. [2004]Schwarz et al. [2008]single particle soot photometer (SP2) (DMT)N/AN/A150 nm to 1.5 μm
Separation of cloud droplets from interstitial aerosolNoone et al. [1988]Ogren et al. [1992]counterflow virtual impactorN/AN/AN/A
Cloud and precipitation size distributionBaumgardner et al. [2001]Cloud, aerosol, and precipitation spectrometer (CAPS)1 s0 – 1,000 particles/cm−30.4 μm to 1.6 mm
Cloud droplet size distributionCerni [1983]forward scattering spectrometer probe (FSSP)1 sN/A1–46 μm
Cloud droplet liquid water contentGerber et al. [1994]light diffraction (Gerber PVM-100 probe)1 sN/A∼5–50 μm
Drop size distributionChuang et al. [2008]Phase-Doppler Interferometer0.1 – 1 sN/A∼2–150 μm
Table A6. CIRPAS Twin Otter Flights
Flight NumberFlight DescriptionDate in 2006
    1Parish power plant plume21 Aug
    2Parish power plant plume22 Aug
    3Parish power plant plume23 Aug
    4Houston Ship Channel area25 Aug
    5Conroe area26 Aug
    6Beaumont area27 Aug
    7Baytown area28 Aug
    8Baytown area28 Aug
    9Parish power plant plume29 Aug
    10Houston Ship Channel area31 Aug
    11Houston Ship Channel area1 Sep
    12Biomass burning2 Sep
    13Houston area3 Sep
    14Parish power plant plume4 Sep
    15Waste treatment plant area6 Sep
    16Galveston area7 Sep
    17Parish power plant plume8 Sep
    18Houston area10 Sep
    19Fayetteville power plant plume11 Sep
    20Conroe area13 Sep
    21Houston area14 Sep
    22Houston area15 Sep

[83] The NASA B200 King Air was instrumented with the NASA LaRC High Spectral Resolution Lidar (HSRL), which measures profiles of aerosol extinction, backscattering, and depolarization throughout the lower and middle troposphere. The HSRL technique [e.g., Shipley et al., 1983] takes advantage of the spectral distribution of the lidar return signal to discriminate aerosol returns from molecular returns and thereby enable independent retrievals of aerosol extinction and backscatter. (Standard backscatter lidars measure a combination of backscatter and extinction, and then retrieve the aerosol components of backscatter and extinction by assuming a value for the extinction-to-backscatter ratio, which can be quite variable.) The LaRC HSRL employs the high spectral resolution technique at 532 nm and the standard backscatter technique at 1064 nm. In addition, the lidar is polarization-sensitive at both wavelengths (i.e., it measures the degree to which the backscatter light is depolarized from the linearly polarized state of the transmitted pulses), which enables discrimination between spherical and nonspherical particles. Hair et al. [2008] provide a detailed description of the NASA LaRC HSRL system.

[84] The LaRC HSRL provided vertically resolved measurements of both extensive and intensive aerosol parameters. Extensive parameters are optical parameters that are influenced by the amount (concentration) and type (size, composition, shape) of aerosol/cloud particles (e.g., extinction). Intensive parameters are those parameters that depend only on the nature of the particles and not on their quantity or concentration (i.e., properties that depend only on aerosol type). These parameters (with approximate nominal horizontal and vertical resolutions) are: (1) extensive parameters, with backscatter coefficient at 532 and 1064 nm (Dx ∼ 1 km, Dz ∼ 60 m), extinction coefficient 532 nm (Dx ∼ 6 km, Dz ∼ 300 m), and layer optical depth at 532 nm (integration of the extinction profile) and (2) intensive parameters, with extinction-to-backscatter ratio at 532 nm (Dx ∼ 6 km, Dz ∼ 300 m), aerosol depolarization ratio at 532 nm and 1064 nm (Dx ∼ 1 km, Dz ∼ 60 m), and aerosol wavelength dependence (Dx ∼ 1 km, Dz ∼ 60 m) (i.e., Ångström exponent for aerosol backscatter, directly related to the backscatter color ratio).

[85] During TexAQS/GoMACCS, the NASA B200 King Air was based at Ellington Field, located about 25 km south of Houston, arrived on 27 August and departed on 28 September. Approximately 78 h of HSRL data were collected on 21 science flights (Table A7). The majority of the flights were over the Houston and Dallas regions; additional flights outside these regions were conducted along the CALIPSO ground tracks to acquire validation data for the CALIOP sensor (Figure A4). Table A7 also shows the flights that were coordinated or coincident with the other aircraft; Terra and/or Aqua MODIS, MISR, CALIPSO overpasses; and contained portions that included overpasses of the Moody Tower and/or NOAA Research Ship Ronald H. Brown.

Figure A4.

Flight tracks of the NASA B200 King Air during TexAQS/GoMACCS. The terrain elevation is qualitatively indicated by the background color.

Table A7. NASA B200 King Air Flightsa
DateFlight NumberBegin Time (UT)End Time (UT)CoordinationComments
  • a

    The boldface letters indicate that a comparison/validation/coordination was conducted: G denotes good degree of success; M denotes moderate or questionable degree of success. CALIPSO validation flights are indicated as day (D) or night (N); MODIS coincidences are indicated as over land (L) or water (W). Platform Abbreviations: RHB, Ronald H. Brown; P3, NOAA WP-3D; NTO, NOAA Twin Otter; CTO, CIRPAS Twin Otter.

27 Aug117011911         Transit flight from NASA Langley to Houston
 220212152         Transit flight from NASA Langley to Houston
28 Aug318412013   GGG DG W  CALIPSO validation flight. Observed Saharan dust.
29 Aug415011819GM  M  L WMRaster scan of Houston
31 Aug516061839G  MM  G L WGRaster scan of Houston area and MISR local mode.
3 Sep615191827   M   M L W Flight over Gulf; highest observed aerosol optical thickness
4 Sep718112127GG  GG DG L W  CALIPSO validation flight
6 Sep818312139    GG DG L W  CALIPSO validation flight east of Houston
7 Sep916021924G  G   G L WGRaster scan over Houston and MISR local mode box
8 Sep1016021924   M     Coordinated NTO track on LA-TX border and Dallas
13 Sep1118372149  GG G DG L  CALIPSO validation track to Dallas and scan of Dallas
14 Sep1216331852G   M   MRaster scan of Houston and MISR local mode box
15 Sep1317002024M M M    Tight raster pattern over Houston
17 Sep1406420931     G N   Night CALIPSO flight over Arizona and Louisiana
 1510551334     G N   Night CALIPSO flight over Arizona and Louisiana
19 Sep1616542038G G      Raster scan of Houston
20 Sep1717502136  M  G DG L W  CALIPSO validation flight west of Houston to Dallas
21 Sep1817232038  G      Raster pattern over Houston coordinated with P3
22 Sep1917552139     G DG L  CALIPSO validation flight to Lincoln, Nebraska
24 Sep2006370937     G N   CALIPSO validation flight and return to Houston
25 Sep2119542242G G   M  Raster pattern over Houston coordinated with P3
26 Sep2218052120  G   M  Raster pattern over Houston coordinated with P3
27 Sep2316572059     G DM  CALIPSO validation flight west of Dallas
28 Sep2414451608     G DM  Transit flight to NASA Langley with CALIPSO track en route
 2517392039     G DM  Transit flight to NASA Langley with CALIPSO track en route

[86] The HSRL also measured daytime planetary boundary layer (PBL) heights through an automated technique using a Haar wavelet covariance transform to identify the sharp gradients in aerosol backscatter located at the top of the boundary layer [Brooks, 2003]. Following the convention used by Davis et al. [2000] and Cohn and Angevine [2000], the altitude of the maximum covariance was used to identify the boundary layer height. The algorithm was modified for the TexAQS/GoMACCS region by: (1) limiting the altitude range to find the PBL height based on the PBL heights from the previous minute, (2) identifying the gradient at lowest altitude which exceeds a threshold, rather than the largest gradient, and (3) increasing the dilation values used in the wavelet analysis. PBL heights were also obtained by visual inspection of the HSRL backscatter profiles; the heights derived from the modified wavelet algorithm and from visual inspection of the HSRL backscatter images agreed to within 10 m in 85% of the cases examined during the study. Entrainment zone thickness was derived as the distance between the 15th and 85th percentiles of the lidar-derived boundary layer heights as per Cohn and Angevine [2000].

[87] A wide variety of satellite-borne instrumentation was integrated into the analysis conducted during TexAQS II/GoMACCS. This analysis included both providing evaluations of the satellite data themselves through comparisons with simultaneously collected in situ data, and including those data in scientific analyses. Section 3.4 summarizes some of this analysis. Table A8 summarizes the characteristics of the satellite instrumentation.

Table A8. NOAA and NASA Satellites and Their Measurement Capabilities
Satellite Platform: Web SiteRelevant InstrumentsRelevant Data ProductsVertical Resolution
  • a

    Available in near-real-time for post flight analysis.

  • b

    Available in real-time for chemical/aerosol data assimilation studies.

NASA Aura: http://aura.gsfc.nasa.govHIRDLS MLS TESa OMIbO3, HNO3, and aerosol extinction1.25 km (UT/LS profiles)
O3, CO, ClO, BrO, HCl, OH, HO2, HNO3, HCN, and N2O1.5–3 km (UT/LS profiles)
O3, CO, CH46 km (tropospheric profiles)
O3, NO2, SO2, HCHO, BrO, OClO, and aerosol characteristicscolumn
NASA Aqua: http://aqua.nasa.govMODISb AIRSa CERESaerosol optical depth, fine mode fraction, fire detectioncolumn, surface
O3, CO, T, Q6 km (UT/LS Profiles)
solar, terrestrial, and total TOA radiation and fluxesTOA, Surface
NASA Terra: http://terra.nasa.govMOPITT MISR MODISbCO6 km (tropospheric profiles)
aerosol optical depth, composition, sizecolumn
aerosol optical depth, fine mode fraction, fire detectioncolumn, surface
NASA CALIPSO: http://www-calipso.larc.nasa.gov/CALIOPaaerosol backscatter ratio, extinction, height120 m (Z < 20 km) 360 m (Z > 20 km)
NOAA GOES-12: http://www.oso.noaa.gov/goes/Geostationary ImagerVisible imagerycolumn
GOES Aerosol/Smoke Product (GASP) Aerosol optical depthcolumn
Wildfire Automated Biomass Burning Algorithm (WF-ABBA)surface
NOAA POES: http://www.oso.noaa.gov/poes/AVHRR TOVS SBUV/2aerosol optical depthcolumn (ocean only)
land coversurface
atmospheric temp15 layers (sfc-0.4 mbar)
precipitable water3 trop layers
precipitation, soil moisturesurface
O312 layers (sfc-1 mbar)

[88] The 22-site Intercontinental Transport Experiment (INTEX) Ozonesonde Network Study (IONS-06) launched sondes during July through September, 2006. Table A9 summarizes the launches. Ozone was determined with electrochemical concentration cells; standard radiosondes, usually RS-80 or RS-92 Vaisala instruments, collected pressure-temperature and below 100 hPa, relative humidity, at 5–10 m resolution. The ozonesondes cover surface to 10 hPa or above with 50- to 100-m resolution in ozone partial pressure; all profiles are archived at http://croc.gsfc.nasa.gov/intexb/ions06.html.

Table A9. IONS-06 Ozone Sonde Stations in Summer 2006
StationLatitude, LongitudeSummer Period (Number Launched)
Barbados13.2, −59.519 Jul to 30 Aug (27)
Beltsville, Md.a39.0, −76.51–28 Aug (12)
Boulder, Colo.40.3, −105.214 Jul to 31 Aug (34)
Bratt's Lake, Sask.50.2, −104.71–30 Aug (29)
Egbert, Ont.a44.2, −79.81–30 Aug (15)
Holtville, Calif.32.8, −115.47–31 Aug (13)
Houston, Tex.a29.7, −95.41–31 Aug (19)
Huntsville, Ala.a35.3, −86.61 Aug to 2 Sep (30)
Kelowna, B. C.49.9, −119.42–30 Aug (27)
Narragansett, R. I.a41.5, −71.418 Jul to 30 Aug (30)
Paradox, N. Y.43.9, −73.630 Jun to 30 Aug (8)
R/V Ronald H. BrownGulf of Mex.31 Jul to 11 Sep (35)
Sable Is, N. S.a44.0, −60.01–31 Aug (28)
Socorro, N. M.36.4, −106.91 Aug to 9 Sep (26)
Stonyplain, Alberta53.6, −114.19–30 Aug (4)
Trinidad Head, Calif.a40.8, −124.227 Jul to 31 Aug (31)
Table Mountain, Calif.34.4, −117.71–31 Aug (30)
Mexico City19.4, −98.622 Aug to 20 Sep (22)
Valparaiso, Indiana41.5, −87.02–31 Aug (5)
Wallops Is, Va.a37.9, −75.52–30 Aug (11)
Walsingham, Ont.42.6, −80.614–25 Aug (22)
Yarmouth, N. S.a43.9, −66.12–30 Aug (13)

Appendix B:: Surface Site Networks

[89] Figure B1 shows the location of sites in the Surface Air Quality Monitoring Network for the TexAQS II campaign, and Table B1 summarizes the measurements conducted at sixteen sites specifically added to the surface site network for TexAQS II. These sites measure a variety of air pollutant concentrations and the data are archived at http://www.tceq.state.tx.us/compliance/monitoring/air/monops/hourly_data.html.

Figure B1.

Map of air pollutant measurement sites, maintained by the TCEQ. Triangles indicate the approximately 100 continuously operating sites, and red stars indicate sites added for TexAQS II to improve the characterization of regional transport of air pollutants.

Table B1. Locations and Measurements of the 16 Surface Sites Specially Deployed by TCEQ for the TexAQS II Studya
CAMSSite DescriptionSurface MeasurementsLatitudeLongitude
  • a

    Abbreviations: CAMS, Continuous Ambient Monitoring Stations; met, surface wind, temperature, and humidity measurements; neph, 3 wavelength nephelometer; 2.5 filter, PM2.5 mass measurements by filter collection; and teom, PM 2.5 mass measurements by Tapered Element Oscillating Microbalance.

C638Smith Point Hawkins CampOzone, met29.546−94.787
C639Newton NTRDOzone, met30.885−93.742
C645Wamba NTRDOzone, met33.500−94.120
C646San Augustine Airport NTRDOzone, neph, met, 2.5 filter31.539−94.170
C648Clarksville NTRDOzone, neph, met, 2.5 filter33.620−95.060
C641Beeville AirportOzone, met28.360−97.790
C649HalletsvilleOzone, met29.447−96.933
C650Italy High SchoolOzone, met32.178−96.878
C651TempleOzone, met30.998−97.339
C652Wichita Falls TexAQSIIneph, met, 2.5 filter33.870−98.460
C653Millpond Park San Sabaneph, met, 2.5 filter31.187−98.712
C654HamshireOzone, neph, NOx, 2.5 teom, met29.864−94.318
C655Eagle Passneph, 2.5 teom, met28.702−100.451
C647PalestineOzone, met31.779−95.706
C657Port O ConnorOzone, 2.5 teom, met28.434−96.455
C667Isla BlancaOzone, neph, met26.073−97.167

[90] The Radar Wind Profiler Network comprised 10 land-based, one oil platform-based, and one shipboard 915-MHz Doppler radar wind profilers [Carter et al., 1995] that measured winds in the planetary boundary layer (see Figure B2 and Table B2). Typical vertical coverage was from 120 m to ∼4000 m above the surface, depending on atmospheric conditions. Radio acoustic sounding systems (RASS) were operated in conjunction with most of the wind profilers to measure temperature profiles up to ∼1500 m. The vertical resolutions of both the wind and temperature measurements were either 60 m or 100 m. The wind profiler data were quality controlled after the data collection period using the continuity technique developed by Weber et al. [1993].

Figure B2.

Map of observing sites (blue squares) in the TexAQS II boundary layer radar wind profiler network. Red circles indicate Texan urban areas.

Table B2. Locations of Boundary Layer Radar Wind Profilers Deployed for the TexAQS II Studya
  • a

    Radio acoustic sounding system.

Arcola, Tex.ACL29.51−95.4821 myesNOAA
Beaumont–Port Arthur, Tex.BPA30.10−94.1024 mnoTCEQ
Beeville, Tex.BVL28.37−97.8075 myesNOAA
Brazos A-19 Oil Platform in the Gulf of MexicoBRZ28.20−95.6024 mnoSonoma Technology
Brenham, Tex.BHM30.22−96.3794 myesNOAA
Cleburne, Tex.CLE32.35−97.44250 mnoTCEQ
Huntsville, Tex.HVE30.72−95.64101 myesNOAA
LaPorte, Tex.LPT29.61−95.178 mnoTCEQ
Longview, Tex.LVW32.38−94.71106 myesNOAA
Moody, Tex.MDY31.34−97.31250 myesNOAA
New Braunfels, Tex.NBF29.70−98.12195 myesSonoma Technology
R/V Ronald H. BrownRHBvariablevariable5 mnoNOAA

[91] Operation of the wind profiler on the R/V Ronald H. Brown was hindered by sea clutter (i.e., sidelobe reflections from the ocean surface), which often prevented wind retrievals in approximately the lowest 500 m above the surface. A Doppler lidar on the Ronald H. Brown measured winds below clouds with up to 5 m resolution using the velocity-azimuth display (VAD) technique [Browning and Wexler, 1968].

[92] During TexAQS II, NOAA maintained an Internet-based air mass trajectory tool [White et al., 2006] that used real-time observations from the profiler network to calculate forward or backward trajectories. The NOAA wind profiler trajectory tool user interface is available at http://www.etl.noaa.gov/programs/2006/texaqs/traj/. The trajectory tool was used during the study to assist with mission planning and after the study to help scientists understand regional transport patterns and pollution source apportionment.

[93] Most meteorological observations have been collected and made available through the Texas A&M University web site, http://atmo.tamu.edu/texaqs2/. In addition to data, the Web site includes quick-look maps and images along with descriptions of the meteorology and ozone during days of particular interest.


[94] The Air Quality and the Climate Research and Modeling Programs of the National Oceanic and Atmospheric Administration (NOAA) and the Texas Commission on Environmental Quality (TCEQ) supported the WP-3D, O3 Lidar aircraft, and Ronald H. Brown R/V measurements. The CIRPAS Twin Otter was supported by the NOAA Climate Program Office under grant NA06OAR4310082. Support for the HSRL deployment and analyses of data was provided by the NASA Science Mission Directorate, the NASA CALIPSO project, the Texas Commission on Environment Quality (TCEQ), and the Office of Science (BER), U. S. Department of Energy (Atmospheric Science Program), Interagency Agreement DE-AI02-05ER6398.