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Ozone-Induced Stipple on Plants in the Cape Romain National Wildlife Refuge, South Carolina
Donald D. Davis

Southeastern Naturalist, Volume 8, Number 3 (2009): 471–478

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2009 SOUTHEASTERN NATURALIST 8(3):471–478 Ozone-Induced Stipple on Plants in the Cape Romain National Wildlife Refuge, South Carolina Donald D. Davis* Abstract - During 1996–1998 and 2002–2003, field surveys were conducted within the Cape Romain National Wildlife Refuge, located on the Atlantic coast of South Carolina, to determine if refuge vegetation exhibited foliar symptoms (stipple) induced by ambient ozone. Foliar stipple was observed on Rhus copallina (Winged Sumac), Sapium sebiferum (Chinese Tallowtree), and Vitis sp. (wild grape). Grape had the greatest frequency of stippled plants, followed by Winged Sumac and Chinese Tallowtree. Chinese Tallowtree produced the most classic ozone-induced stipple, and may have the most potential as a useful ozone-sensitive bioindicator. Percentage of plants with ozone-induced symptoms varied among species and years. The threshold value of CUM60 ambient ozone needed to induce symptoms on ozonesensitive plants in the refuge was estimated to be approximately 9000 ppb-hrs. Introduction The Cape Romain National Wildlife Refuge (Cape Romain NWR), administered by the US Fish and Wildlife Service (USFWS), was established in 1932 as a migratory bird refuge. The 25,993-ha refuge, part of the Carolinian- South Atlantic Biosphere Reserve, is located along the Atlantic coast of southeastern South Carolina and is managed to provide quality habitat for a diversity of wildlife species. Most of the refuge is located on Bull Island, an ancient barrier reef approximately 10 km long and 3 km wide, but the refuge also encompasses several ha on the mainland. The Cape Romain NWR contains barrier islands, salt marshes, coastal waterways, beaches, fresh and brackish water impoundments, and maritime forests (unpublished USFWS brochures). In 1975, Congress conferred wilderness status on 11,331 ha of the Cape Romain NWR and designated the “Cape Romain Wilderness” as a Class I air quality area, affording the area stringent protection under the Clean Air Act as amended in 1977 (US Congress 1977). The act gave federal land managers of Class I areas the responsibility to protect all air quality related values (AQRVs), including vegetation, wildlife, water, soils, visibility, and cultural resources. By federal law, AQRVs in Class I areas must be protected from deterioration. However, despite special protection, Class I air quality areas in eastern US have been adversely affected by ozone (Chappelka et al. 2003; Davis 2007a,b; Davis and Orendovici 2006; Lefohn and Manning 1995; Manning et al. 1996). In order to determine if deterioration is occurring, baseline AQRVs must be established. Therefore, the overall *Department of Plant Pathology and Penn State Institutes of Energy and the Environment, The Pennsylvania State University, University Park, PA 16802; 472 Southeastern Naturalist Vol. 8, No. 3 objective of this survey was to determine if vegetation within the Cape Romain NWR was being injured by ambient ozone, and if so, to what extent it was occurring in the refuge. Specific objectives were to: 1) determine if vegetation within the refuge was exhibiting foliar symptoms induced by ambient ozone; 2) determine the incidence (percentage) of ozone-sensitive, bioindicator plants exhibiting symptoms; and 3) if datasets were sufficient, determine if incidence of ozone symptoms was related to species, ambient ozone levels, and drought stress. This paper is the fourth in a series dealing with ozone injury on vegetation within US national wildlife refuges (Davis 2007a,b; Davis and Orendovici 2006). Methods Stalter (1984) identified 268 species of native and introduced plants in the Cape Romain NWR, and Helm et al. (1991) characterized the maritime forest within the refuge. A species list of vegetation compiled by refuge personnel was given to the author prior to the initial survey in 1996. From this list, the author noted that the refuge contained several ozone-sensitive bioindicators (later summarized in USDOI 2003), including Rhus copallina L. (Winged Sumac) and Vitis spp. (wild grape). Bioindicators are broadleaved, ozone-sensitive plants that respond to ambient ozone by producing characteristic, diagnostic adaxial “stipple,” as first described by Richards et al. (1958) and illustrated by Skelly (2000). Ambient ozone is monitored within the Cape Romain NWR at EPA AIRS Site #45-019-0046. The National Park Service, Denver, CO, provided the EPA ozone data for several years prior to the initial 1996 survey. These datasets revealed elevated levels of ambient ozone occurred within the refuge. This information, along with the presence of potential ozone-sensitive bioindicators in the refuge, provided the impetus for these surveys. Vegetation in the Cape Romain NWR was surveyed during late summer in 1996–1998 and 2002–2003 on the dates listed in Table 1. Methods were similar to those used by the author in other wildlife refuges (Davis 2007a,b; Davis and Orendovici 2006). Prior to the initial survey in 1996, refuge maps were examined to identify open areas with unrestricted air movement and sunlight, criteria for suitable survey areas (Anderson et al. 1989). Potential locations were visited in early 1996. At this time, it was observed that wild grape and Winged Sumac occurred frequently within the open areas along access roads and at the refuge boat landing. It was also noted that Sapium sebiferum (L.) Roxb. (Chinese Tallowtree) was very abundant in the refuge, especially in wet areas. Anderson et al. (1986) had reported that Chinese Tallowtrees on the eastern half of Bull Island exhibited symptoms resembling those caused by ozone. Therefore, this species was added to the list as a possible bioindicator. Other potential bioindicators were noted in the field, but they were generally few in number and scattered. 2009 D.D. Davis 473 Based on these initial observations, the author selected those open survey areas on Bull Island and within the mainland portion of the refuge that contained the greatest numbers of Chinese Tallowtree, wild grape, and Winged Sumac. At each survey area, the author counted the number of Chinese Tallowtree, wild grape, and Winged Sumac plants, and recorded the number of stippled plants within each species. Stipple was noted simply as present or absent on individual bioindicator plants; severity (percent symptomatic leaf tissue) of stipple was not evaluated. Percentage (incidence) of plants exhibiting stipple within each of the three plant species was calculated. Since species (USDOI 2003), ozone level (Hildebrand et al. 1996), and drought stress (Eckert et al. 1999, Showman 1991, Yuska et al. 2003) infl uence visible ozone-symptom expression, the author investigated the relationship among these factors and incidence of stipple using binomial logistic regression (Davis and Orendovici 2006, Minitab 2003). Bioindicator species were numbered from 1–3. Annual ambient ozone levels were expressed as CUM60 (ppb-hrs), the cumulative sum of all hourly ozone concentrations ≥60 ppb, 24 hrs/day, during the time period from January 1 to the first day of each year’s survey. Annual soil moisture as of July 31 of each survey year was expressed as the Palmer Drought Severity Index (PDSI), an approximation of drought stress based mainly on soil moisture and temperature (Palmer 1965). PDSI was calculated using data for the southeastern coast of South Carolina (USNCDC 2004). CUM60 ozone levels for April through September of each survey year were graphed to illustrate temporal ozone patterns during the growing season (Fig 1). Results and Discussion Foliar symptoms Ozone-induced stipple was observed on at least two of the bioindicator species during each survey year, and all species exhibited classic adaxial foliar injury (Richards et al. 1958, Skelly 2000). Relative prevalence of and mean percentage (in parentheses) of individuals exhibiting stipple across all years were: wild grape (32.7%) > Winged Sumac (16.8%) > Chinese Tallowtree (8.6%), as shown in Table 1. Wild grape and Winged Sumac were also reported to be useful ozone-sensitive bioindicators in the Edwin B. Forsythe NWR in New Jersey (Davis and Orendovici 2006). However, grape foliage in both refuges exhibited late-summer insect injuries that complicated evaluation of ozone-induced symptoms. Similarly, Winged Sumac foliage became red during late summer in both refuges, complicating stipple evaluation, and could not be utilized in the Cape Romain NWR in 1998 and 2003 (Table 1). Photographic images of stipple on wild grape and Winged Sumac were taken, but quality was not high enough for publication. Although Chinese Tallowtree was asymptomatic in 1996, this species produced classic, easily discernable stipple (Fig. 2) in other years, and exhibited little insect injury or foliar reddening. Anderson et al. (1986) reported that Chinese Tallowtrees on Bull Island exhibited symptoms resembling those 474 Southeastern Naturalist Vol. 8, No. 3 Figure 2. Classic ozone-induced stipple on the upper surface of a Chinese Tallowtree leaf from the Cape Romain NWR. Figure 1. Cumulative sum of hourly ozone concentrations ≥60 ppb (CUM60, ppbhrs) monitored within the Cape Romain NWR at EPA AIRS Site # 45-019-0046 beginning April 1 during survey years (1996–1998 and 2002–2003). Monitored ozone data furnished by David Joseph, National Park Service, Denver, CO. 2009 D.D. Davis 475 caused by ozone, but cautioned, “We do not have any fumigation data on this species and cannot be sure if the observed symptoms were ozone caused.” However, based on their symptom description and the author’s observations, it is likely that symptoms observed by Anderson et al. were caused by ozone. Chinese Tallowtree warrants consideration for use as an ozone bioindicator in southern refuges. This assumption should be confirmed in controlled exposure studies. Ambient ozone concentrations Annual, ambient, cumulative ozone concentrations (CUM60, ppbhrs) as of the first day of survey each year were: 24,437 ppb-hrs (1997) > 22,668 ppb-hrs (2002) > 17,769 ppb-hrs (2003) > 17,424 ppb-hrs (1998) > 9216 ppb-hrs (1996). Within a growing season, ozone concentrations followed similar patterns each year, gradually increasing from April to the end of summer and then leveling off in September (Fig. 1). In comparison to other wildlife refuges surveyed by the author, ambient ozone concentrations in the Cape Romain NWR were greater than in the remote Seney NWR in northern Michigan (Davis 2007b), but somewhat less than those at Brigantine NWR in New Jersey (Davis and Orendovici 2006), Moosehorn NWR in Table 1. Summary of observations made during the 1996–1998 and 2002–2003 surveys at the Cape Romain NWR. Numbers within species columns refer to number of plants exhibiting ozone-induced stipple as compared to the total number of plants evaluated for that species; data also expressed as percentages. Ozone values are expressed as CUM60 (ppb-hrs) as of the first day of survey for each year. Drought is expressed as Palmer drought severity index (PDSI) as of July 31 in each survey year. Blank spaces in species columns indicate no data. Species CUM60 Wild Winged Chinese Weighted ozone PDSI Survey date/no. plants grape Sumac Tallowtree average (ppb-hrs) (index) 1996 (Aug 21–24) Number plants examined 56 45 273 Number plants stippled 14 5 0 Percentage 25.0% 11.1% 0.0% 5.08% 9216 -1.17 1997 (Aug 13–18) Number plants examined 54 73 107 Number plants stippled 24 14 30 Percentage 44.4% 19.2% 28.0% 29.06% 24,437 1.23 1998 (Aug 18–20) Number plants examined 33 105 Number plants stippled 12 23 Percentage 36.4% 21.9% 25.36% 17,424 -3.05 2002 (Sept 9–11) Number plants examined 41 25 108 Number plants stippled 13 5 5 Percentage 31.7% 20.0% 4.6% 13.22% 22,668 0.27 2003 (Sept 3–5) Number plants examined 15 116 Number plants stippled 2 3 Percentage 13.3% 2.6% 3.82% 17,769 2.45 Weighted average 32.66% 16.78% 8.60% 476 Southeastern Naturalist Vol. 8, No. 3 Maine (Davis 2007a), and the Mingo NWR in Missouri (D.D. Davis, unpubl. data). Ozone data at the latter two NWRs were inferred from the EPA monitoring site nearest each refuge. Ozone, or its precursors, may be produced in urban or industrial areas southwest of the refuge and transported to the Cape Romain NWR on southwesterly winds. Based on the 1996 observations, the threshold CUM60 ozone level needed to induce symptoms on sensitive plants within the Cape Romain refuge is likely near 9000 ppb-hrs. If so, ozone injury might have occurred on sensitive plants in the refuge as early as June in 2002 and 2003 when this threshold was exceeded (Fig. 1). Injured leaves from June–July exposures may defoliate or become hidden by new growth, and may not be evident during the mid- to late-August period, when ozone-injury surveys are usually conducted. In addition, high ozone levels in late spring or early summer may cause injury to plant species that emerge and complete their life cycles early in the growing season, such as late-spring or early-summer ephemerals (Davis and Orendovici 2006) or other early successional species (Barbo et al. 1998); such injury would likely not be evident during mid- to late-August surveys. The binary logistic model was not used to examine relationships among species, ozone levels, and drought since the Pearson’s (chi-square) goodness-of-fit statistic was not significant (Minitab 2003). Lack of significance was likely influenced by the small dataset, as well as confounding relationships between ambient ozone levels and environmental factors. In summary, foliar symptoms caused by ambient ozone were observed on bioindicator plants within the Cape Romain NWR during each survey year. It is likely that ozone levels are great enough during most years to cause injury to sensitive plants within the refuge, including those growing within the Class I Wilderness air quality area. The US Fish and Wildlife Service may utilize the results of these surveys when making air quality management decisions, including those related to review of Prevention of Significant Deterioration permits. Such survey data may be used as input to strengthen our National Ambient Air Quality Standards for ozone (USEPA 2007). Acknowledgments The author gratefully acknowledges receiving financial support from the US Fish and Wildlife Service, Air Quality Branch, Denver and the Pennsylvania Department of Environmental Protection, Bureau of Air Quality, Harrisburg. The author also thanks Mr. David Joseph, National Park Service, Denver for furnishing the ambient ozone datasets. Literature Cited Anderson, R.L., C. Scarrow, and J.L. Knighten. 1986. 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