SOUTHERN COASTAL SANTA BARBARA STREAMS AND ESTUARIES BIOASSESSMENT PROGRAM

2014 REPORT AND UPDATED INDEX OF BIOLOGICAL INTEGRITY

Prepared for:

City of Santa Barbara, Creeks Division

County of Santa Barbara, Project Clean Water

Prepared By:

www.ecologyconsultantsinc.com

Ecology Consultants, Inc.

Executive Summary Introduction This report summarizes the results of the 2014 Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program, an effort funded by the City of Santa Barbara and County of Santa Barbara. This is the 15th year of the Program, which began in 2000. Ecology Consultants, Inc. (Ecology) prepared this report, and serves as the City and County’s consultant for the Program. The purpose of the Program is to assess and monitor the “biological integrity” of study streams and estuaries as they respond through time to natural and human influences. The Program involves annual collection and analyses of benthic macroinvertebrate (BMI) samples and other pertinent physiochemical and biological data at study streams using U.S. Environmental Protection Agency (USEPA) endorsed rapid bioassessment methodology. BMI samples are analyzed in the laboratory to determine BMI abundance, composition, and diversity. Scores and classifications of biological integrity are determined for study streams using the BMI based Index of Biological Integrity (IBI) constructed by Ecology. The IBI was initially built in 2004, updated in 2009, and has been updated again this year. The IBI yields a numeric score and classifies the biological integrity of a given stream as Very Poor, Poor, Fair, Good, or Excellent based on the contents of the BMI sample collected from the stream. Several “core metrics” are calculated and used to determine the IBI score. Each core metric is highly sensitive to human disturbance as determined through rigorous statistical analyses of data from local streams. Collectively, the core metrics represent different aspects of BMI community structure including diversity, composition, and trophic group representation. By condensing complex biological data into an easily understood score and classification of biological integrity, the IBI serves as an effective tool for the City and County in monitoring the condition of local streams, and evaluating the benefits or consequences of watershed management actions. In 2011 the Program was expanded to include the study of local estuaries. Estuaries are open water bodies where a freshwater stream meets and mixes with saltwater from the ocean, creating brackish water conditions with salinities that change depending on varying seasonal inputs from the stream and ocean. USEPA endorsed rapid bioassessment methods for estuaries were used to collect BMI samples and other pertinent physiochemical and biological data. Over the past four years, a relatively limited data set has been compiled for local estuaries. Study sites have included the range available along a disturbance gradient, from “reference” sites that are fairly intact in form with little urbanization in their watersheds to “highly disturbed” sites that have been substantially altered in form and drain highly urbanized watersheds. Intermediate “moderately disturbed” sites have also been surveyed. A major goal in studying local estuaries is to identify several reliable BMI indicator metrics that show significant differences trends along a disturbance gradient. Such indicator BMI metrics will be the foundation in developing a reliable IBI for local estuaries. Study Area The study area encompasses approximately 80 km of the southern Santa Barbara County coast from the Rincon Creek watershed at the Santa Barbara/Ventura County line west to Jalama Creek just north of Point Conception. There are approximately 50 1st to 5th order coastal

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Ecology Consultants, Inc. streams along this stretch of coast, all of which drain the southern face of the Santa Ynez Mountains. 49 different stream study reaches in 20 watersheds have been surveyed on one or more occasions from during the 15 years of the Program, while 10 different estuaries have been studied once or more over the last 4 years. Results Over the past 15 years, the Program has provided a wealth of information regarding the physiochemical habitat conditions and biota (particularly the BMI community) present in local streams. The influences of natural physiochemical and climatic variability and human development on local stream communities have been extensively examined. The following statements can be made based on the research completed thus far: • The updated IBI is highly effective as an indicator of biological integrity, with highly significant relationships with indicies of human disturbance. The IBI has properly differentiated between reference (REF), moderately disturbed (MOD DIST), and highly disturbed (HIGH DIST) study reach groups at a significant level for each year of the Program. • Negative impacts of human land use on local stream communities (particularly BMIs) have been documented with highly significant statistical test results. Degradation of stream communities (e.g., lower IBI scores and loss of sensitive species), as well as physiochemical habitat conditions, has increased linearly with increased watershed development. Urban development has been shown to have greater impacts on stream communities than has agricultural development. • Major episodic disturbances including extreme stream flows, drought conditions, and wildfires have been definitively shown to negatively impact stream communities, as evidenced by lower IBI scores and loss or significant reduction of sensitive BMI and vertebrate taxa following such events. Local stream BMI communities have proven to be resilient, typically showing dramatic recovery from extreme episodic disturbances in a year or two. However, some of the more sensitive species (e.g., rainbow trout) have yet to return to streams impacted by recent wildfires, and may require many years to recover. • Stream habitat restoration sites M2 and AB5 have shown improved habitat conditions, but significant improvements in the BMI community have not occurred thus far at these sites. Channel and riparian restoration at these sites did not address larger scale impairments in hydrology, geomorphology, water quality, habitat continuity and connectivity that have resulted from alteration of their respective watersheds. Much of this watershed-scale impairment cannot be undone from a practical sense. Whether or not current and future restoration efforts will improve the BMI community at M2 and AB5 can only be evaluated via continued monitoring through time. The Program effort to study local estuaries is still relatively new. Based on the limited data set available, the following can be stated thus far: • Seven BMI metrics appear to have promise as indicators of biological integrity for salinities between 0-30 ppt, with significantly different mean abundances between reference and highly disturbed sites. Some or all of these BMI metrics may be suitable

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for use as core metrics in an estuarine IBI that could be developed in the future. % sensitive BMIs and % tolerant BMIs thus far have the greatest potential, both of which have been significantly different between reference and highly disturbed estuaries in each year of study despite wide physiochemical variability from year to year caused by variable rainfall and freshwater inputs. • While salinity certainly has major influences on the composition of the BMI community in local estuaries (i.e., the specific taxa present), thus far it has had no significant effects on any of the potential core BMI metrics within the range of 0-30 ppt. More replication and diversification of reference estuaries having greater physiochemical variability will be needed to gain more confidence in our ability to understand the influences of salinity and other physiochemical parameters on potential indicator BMI metrics. Understanding natural physiochemical influences will be a key step in evaluating the suitability of potential core BMI metrics for inclusion in a future estuarine IBI. • Four of the estuaries surveyed this past year had bottom salinities of greater than 30 ppt. This was the first time that salinities of this level were present in study estuaries. The four high salinity estuaries surveyed include one moderately disturbed and three highly disturbed sites. The four estuaries having salinity of greater than 30 ppt had different BMI composition by disturbance group compared to all the other estuaries. Salinity may become the dominant determining factor of BMI composition where it exceeds 30 ppt. More study of high salinity estuaries, and reference sites in particular, will be needed to further explore this. • Developing a reliable IBI for local estuaries is a major goal of this Program. Accomplishing this will require a greater understanding of relationships between potential core BMI metrics, human disturbance, and the effects of natural physiochemical variables. Based on the progress made thus far, it is hoped this goal will be attained through another two or three years of study.

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TABLE OF CONTENTS

Page I. INTRODUCTION ...... 7 II. STUDY AREA ...... 14 III. METHODS ...... 20 A. Field Surveys ...... 20 B. Laboratory Analysis ...... 22 C. GIS Analyses ...... 23 D. Review of Topographic Maps and Aerial Photographs ...... 23 E. Study Reach Grouping ...... 23 F. Data Analyses for Streams ...... 24 G. Data Analyses for Estuaries ...... 34 IV. RESULTS AND DISCUSSION ...... 37 A. Physiochemical and Biological Data ...... 37 B. Streams Data Analyses ...... 37 C. Estuaries Data Analyses ...... 57 V. CLOSING ...... 63 VI. ACKNOWLEDGEMENTS ...... 64 VI. REFERENCES ...... 65

APPENDIX A: DATA TABLES APPENDIX B: ESTUARY HABITAT ASSESSMENT SCORING SHEET

PLATES Page Plate 1 Pristine Stream Reach Example ...... 12 Plate 2 Disturbed Stream Reach Example ...... 13 Plate 3 Jesusita Fire Map ...... 33

FIGURES Page Figure 1 Study Area ...... 16 Figure 2 Gaviota Coast Study Reaches...... 17 Figure 3 Santa Barbara and Goleta Area Study Reaches ...... 18 Figure 4 Carpinteria Area Study Reaches ...... 19 Figure 5 Tolerance Values Criteria ...... 27 Figure 6 Examples of Tolerance Value Determinations through ANOVA of Individual BMI Taxa...... 38 Figure 7 ANOVA Comparisons of # EPT Families and TV avg. at REF, MOD DIST, and HIGH DIST Reaches ...... 40

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Figure 8 ANOVA Comparison of Updated IBI Score at REF, MOD DIST, and HIGH DIST Reaches ...... 44 Figure 9 Multiple Regression Analyses of Updated IBI Score vs. Human Disturbance Regressors ...... 45 Figure 10 ANOVA Comparison of IBI Score for Wet, Moderate, and Dry Rainfall Groups 47 Figure 11 ANOVA Comparison of IBI Score by Year for REF Streams ...... 48 Figure 12 ANOVAs of IBI Score for HIGH DIST, MOD DIST, and REF Disturbance Groups for Selected Years ...... 50 Figure 13 IBI and Habitat Assessment Scores by Year, Disturbance and Fire Category .. 52 Figure 14 Analyses of Habitat Assessment and IBI Scores for Restoration Site M2 and Control Site ...... 55 Figure 15 Analyses of Habitat Assessment and IBI Scores for Restoration Site AB5 and Control Site ...... 56 Figure 16 ANOVAs of Mean Abundance of Selected BMI Taxa in Estuaries for REF, MOD DIST, and HIGH DIST Groups ...... 58 Figure 17 ANOVAs of Mean Abundance of Selected BMI Metrics in Estuaries for REF, MOD DIST, and HIGH DIST Groups ...... 59 Figure 18 Linear Regression of % Sensitive BMIs vs. Salinity, REF Group ...... 60 Figure 19 ANOVAs of % Sensitive BMIs by Disturbance Group and Year ...... 62

TABLES Page Table 1 Study Reaches ...... 14 Table 2 Physiochemical and BMI Metrics Calculated for Study Stream Reaches ...... 25 Table 3 Core Metric Scoring Range Criteria ...... 30 Table 4 IBI Classifications of Biological Integrity and Scoring Criteria ...... 31 Table 5 IBI Accuracy of Classification Criteria ...... 31 Table 6 Physiochemical and BMI Metrics Calculated for Study Estuaries ...... 35 Table 7 Core Metric Scoring Ranges ...... 42 Table 8 IBI Alternatives and Classifications of Biological Integrity ...... 42 Table 9 Accuracy of IBI Alternatives ...... 43

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I. Introduction

This report summarizes the results of the 2014 Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program, an effort funded by the City of Santa Barbara and County of Santa Barbara. This is the 15th year of the Program, which began in 2000. Ecology Consultants, Inc. (Ecology) prepared this report, and serves as the City and County’s consultant for the Program. The purpose of the Program is to assess and monitor the “biological integrity” of study streams and estuaries as they respond through time to natural and human influences. The Program involves annual collection and analyses of benthic macroinvertebrates and other pertinent physiochemical and biological data at study streams and estuaries using United States Environmental Protection Agency (USEPA) endorsed rapid bioassessment methodology. BMI samples are analyzed in the laboratory to determine BMI abundance, composition, and diversity. Scores and classifications of biological integrity are determined for study streams using the BMI based Index of Biological Integrity (IBI) constructed by Ecology. The IBI was initially built in 2004, updated in 2009, and has been updated again this year. What is biological integrity? “Biological integrity” can be defined as “the ability (of a water body) to support and maintain a balanced, integrated, adaptive community of organisms having a species composition, diversity, and functional organization comparable to that of natural habitat of the region.” (Miller et al., 1988). In other words, biological integrity can be thought of as the overall biological condition of a water body in comparison to natural, or pristine, habitat in the same region. Water bodies subject to natural disasters (e.g., heavy floods, droughts, wildfires, etc.) or human disturbance (e.g., to hydrology, geomorphology, water chemistry, etc.) typically have poorer biological integrity compared to more pristine water bodies that are relatively free of large-scale disturbances. How do we determine, or measure, biological integrity? “Bioassessment” is the science of determining, or measuring, the biological integrity of water bodies by evaluating the biological assemblages (e.g., benthic macroinvertebrates, fish, amphibians, vegetation, etc.) that inhabit them. The origins of bioassessment in the United States and Europe date back to the late 1800’s. Within the last 30 years, the incorporation of bioassessment into water monitoring programs has increased dramatically throughout the United States because of the development of rapid, cost-effective assessment and data analysis techniques (Rosenberg and Resh, 1993). Currently, bioassessment is used throughout much of the country to assess, monitor, and manage the integrity of streams, rivers, lakes, ponds, estuaries, and coastal marine waters. Bioassessment is based on the fact that individual aquatic plant and animal species have varying habitat requirements and abilities to withstand natural and human-induced habitat disturbances. The sensitivity of each unique species to habitat disturbances has to do with, among other factors, their physiology, size, habitat requirements, survival strategy (i.e., filter feeder, grazer, predator, etc.), and exposure to pollution and other disturbances. The presence or absence of disturbance sensitive species serves as an indicator of the overall biological integrity a particular water body.

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As an example, the presence of viable salmonid populations in coastal California streams generally indicates good biological integrity. To thrive, salmonids require cool, clean, well-oxygenated stream water, clean cobble/gravel beds for spawning, deep pools for cover from predators, and an adequate aquatic invertebrate and vertebrate prey base. Salmonids are negatively affected by increased fine sediment loads, higher stream temperatures, water pollution, and other habitat modifications such as the construction of dams and other migration barriers that typically occur in areas with intensive human development. While species such as Rainbow trout in Rattlesnake salmonids that are sensitive to habitat disturbances are Creek typically reduced or eliminated in highly disturbed water bodies, disturbance tolerant species may persist or even flourish. Disturbed waters typically have a biological community composed of a smaller number of more disturbance tolerant taxa compared to more natural, pristine waters, which typically have higher numbers of taxa, including those that are disturbance sensitive. Beyond individual species, measurements of the biological community, or “biological metrics”, relating to abundance, species richness, proportion of disturbance sensitive species, and trophic structure have been shown to be reliable indicators of biological integrity in this and many other bioassessment studies (Rosenberg and Resh, 1993, Barbour et al., 1999, Cooper, et al. 2013). The reliability of such metrics as indicators of biological integrity depends on the strength of their relationships with measures of habitat disturbance at the watershed and local level. What is the pattern of human development in the study area, and how does it impact habitat conditions in local streams and estuaries? The current pattern of human development is a mosaic of agricultural and urban land uses of varying intensities spread throughout the study View south above Rattlesnake Canyon area, which encompasses the southern slopes of the Santa Ynez mountains from the Santa Barbara/Ventura County line to Point Conception. In general, human development is minimal in the northern mountainous areas, with some grazing, orchards and light residential uses in the foothills, transitioning to more intensive agriculture and urban development further southward where there are extensive coastal plains. The majority of development is concentrated in the cities of Santa Barbara, Goleta, and Carpinteria. Disturbance is limited mostly to orchards, grazing, and rural residential west of Goleta to Point Conception. Common forms of human caused habitat degradation in local streams and estuaries include: (1) altered hydrology and geomorphology due to water diversions, urban and agricultural land development, and flood control projects; (2) burying of stream and estuary substrate due to

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Ecology Consultants, Inc. increased deposition of fine sediments from eroding agricultural fields and stream banks; (3) loss of riparian and upland habitat essential to many aquatic species; (4) loss of stream and estuary habitat complexity, algal blooms, elevated water temperatures, wider fluctuations in dissolved oxygen, and loss of energy inputs due stream channelization and removal of riparian vegetation; (5) degraded water quality due to inputs of fertilizers, pesticides, petroleum hydrocarbons, heavy metals, and other pollutants; (6) habitat fragmentation and barriers to species movement and migration due to the construction of in-stream barriers such as dams, road crossings, bridges, and culverts; (7) introductions of invasive, non-native plants and animals, which can outcompete and threaten the long-term viability of native species; and (8) disturbances to vegetation and/or wildlife associated with trampling, noise, lighting, air pollution, and predation by domestic pets. Generally, the nature and magnitude of habitat degradation in local streams and estuaries is proportional to the cumulative intensity and extent of development in their watersheds. Plates 1 and 2 provide examples of two stream study reaches: (1) a relatively pristine stream in the undeveloped mountains, and (2) a disturbed stream on the urbanized coastal plain. The plates show the positions of these two stream reaches in their respective watersheds, surrounding land uses, and photographs of stream habitat conditions and aquatic species. What is the streams IBI? What does it tell us? The streams IBI developed through this Program is a multimetric tool that provides a standardized, integrative, and readily BMI sampling understandable method for measuring the biological integrity of local streams. The term multimetric refers to an IBI being constructed by combining several individual biological metrics into a single index. Our IBI focuses on benthic macroinvertebrates (BMIs), and several BMI metrics derived from the BMI samples collected at the study stream reaches. These BMI metrics, called core metrics, are all highly sensitive to human-induced habitat degradation as determined through rigorous statistical analyses, and collectively represent several aspects of BMI community structure including relative abundances of disturbance sensitive and tolerant taxa, taxonomic richness, and trophic structure. Values for each core metric at a study stream are scored on a dimensionless numeric scale (e.g., from 0 to 10) relative to the known distribution of values for sites along a human disturbance gradient based on watershed development patterns and localized habitat conditions. Higher scores (e.g., a 10) represent the conditions at the most pristine sites, whereas lower scores indicate greater departure from pristine conditions. Scores assigned to the individual core metrics are equally weighted and combined into an overall score, or measure, of biological integrity for the study stream. The IBI classifies the biological integrity of a given stream as Very Poor, Poor, Fair, Good, or Excellent based on the overall score. By condensing complex biological data into an easily understood score and classification of biological integrity, the IBI serves as an effective tool for the City and County in monitoring the condition of local streams, devising and prioritizing watershed management actions, and evaluating their benefits or consequences.

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Because biological assemblages vary in response to natural physical and chemical gradients that occur through geographic space, IBIs are calculated for specific regions and water body types (i.e., streams, lakes, estuaries, etc.) with similar ecological characteristics. This minimizes the potential for confusion between the influences of natural physical and chemical variations and human impacts on ecological communities. If necessary, water body classes can be further classified and partitioned based on physical and chemical characteristics such as elevation, gradient, size, and nutrient and productivity levels (Miller et al., 1988, Gerritsen, 1995, Barbour, et al., 1996, Lyons and Wang, 1996, Barbour, et al., 1999, Karr and Chu, 1999, Ode, Rehn, and Harrington, 2002). What are BMIs? IBIs are typically developed for a single assemblage of organisms (e.g., BMIs, fish, amphibians, algae, etc.). Like many other bioassessment studies of wadeable streams, this study uses BMIs as indicators of biological integrity. BMIs are aquatic insects, crustaceans, mollusks, worms, and other invertebrates of a half-millimeter in length or greater that inhabit the bottom substrata of streams, lakes, ponds, estuaries, ocean waters, and other water bodies for at least part of their life cycles (Rosenberg and Resh, 1993). There are several reasons why BMIs are useful as biological indicators. First, BMIs are a critical component of aquatic ecosystems, often representing a Stoneflies and Hemiptera large proportion of community biomass, performing in Gobernador Creek important functions in the cycling of nutrients and energy, and constituting food sources for vertebrate predators such as fish and amphibians (Rosenberg and Resh, 1993; Allan, 1995, Hauer and Lamberti, 1996; Merritt and Cummins, 1996; Barbour et al., 1999). Major changes in BMI assemblages can have profound ramifications for aquatic ecosystems. Secondly, the responsiveness of BMIs to environmental perturbations, including human impacts, is well documented (Rosenberg and Resh, 1993; Allan, 1995, Hauer and Lamberti, 1996; Merritt and Cummins, 1996; Barbour et al., 1999, Cooper et al., 2013). Information is available on the life histories, distributions, habitat requirements, and disturbance tolerances of most BMIs. In the case of wadeable streams, BMIs also are typically more abundant and diverse compared to other groups such as fish and amphibians, and are relatively easy to collect (Rosenberg and Resh, 1993; Hauer and Lamberti, 1996; Merritt and Cummins, 1996; Barbour et al., 1999).

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Estuaries In 2011 the Program was expanded to include the study of local estuaries. Estuaries are open water bodies where a freshwater stream meets and mixes with saltwater from the ocean, creating brackish water conditions with salinities that vary depending on fluctuating seasonal inputs from the stream and ocean. USEPA endorsed rapid bioassessment methods for estuaries were used to collect BMI samples and other pertinent physiochemical and biological data. Tecolote Creek estuary (moderate disturbance)

Over the past four years, a relatively limited data set (i.e., compared to streams) has been compiled for local estuaries. Study sites have included the range available along a disturbance gradient, from “reference” sites that are fairly intact in form with little urbanization in their watersheds to “highly disturbed” sites that have been substantially altered in form and drain highly urbanized watersheds. Intermediate “moderately disturbed” sites have also been surveyed. A total of 10 estuaries were studied this year. A major goal in studying local Mission Creek estuary estuaries is to identify several reliable BMI indicator (high disturbance) metrics that show significant trends along a disturbance gradient. Hopefully, such indicator BMI metrics will be the foundation in developing a reliable IBI for local estuaries within the next two to three years.

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Plate 1: Pristine Stream Reach Example

Stream reach location marked on map (left) by black dot. Upstream watershed drains wilderness lands (olive green and brown in map). Agricultural (light green) and urban (grey) lands (downstream) do not affect this stream reach. Stream has unaltered hydrology and form, with natural bed and banks, alternating riffles and pools, boulder and cobble beds (no excessive fine sediments), and intact mostly native riparian vegetation with mature canopy trees. Stream habitat is optimal for a variety of aquatic and riparian species, including a diverse BMI community and several sensitive aquatic vertebrates including rainbow/steelhead trout, California newt, and southwestern pond turtle (below).

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Plate 2: Disturbed Stream Reach Example

Stream reach location marked on map (left) by black dot. Stream drains urban (grey), agricultural (light green) and wilderness lands (olive green/brown). Impervious surfaces (urban), channelization, and increased fine sediment loads (agriculture) have altered stream hydrology and form, and water pollutants (e.g., nutrients, pesticides, hydrocarbons) are present. Stream banks have been largely denuded of native vegetation, resulting in unstable, eroding banks, establishment of invasive non-native plants (e.g., Arundo donax below), algal blooms, and wide fluctuations in water temperature and dissolved oxygen. Fine sediments largely smother boulder, cobble, and gravel that would provide stable aquatic habitat. Sensitive BMIs and aquatic vertebrates are largely absent due to habitat degradation.

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II. Study Area The study area encompasses approximately 80 km of the southern Santa Barbara County coast from the Rincon Creek watershed at the Santa Barbara/Ventura County line west to Jalama Creek, which is just north of Point Conception (see Figure 1). There are approximately 50 1st to 5th order coastal streams along this stretch of coast, all of which drain the southern face of the Santa Ynez Mountains. 49 different stream study reaches in 20 watersheds have been surveyed on one or more occasions from during the 15 years of the Program, while 10 different estuaries have been studied once or more over the last 4 years. Table 1 lists all of the stream reaches and estuaries studied. Figure 1 shows an overall map of the study area, and Figures 2, 3, and 4 provide more detailed maps and show the locations of the stream and estuary study reaches that have been surveyed over the years (except the Jalama Creek estuary).

Table 1: Study Reaches

Study Reach Location RIN0 Rincon Creek just upstream of Rincon Rd. crossing RIN1 Rincon Creek, just upstream of Highway 150 crossing at Gobernador Cyn Rd. C1 Carpinteria Creek, 0.25 mi. downstream of Carpinteria Ave. C2 Carpinteria Creek, approx. 0.25 mi. upstream of U.S. 101 C3 Gobernador Creek, approx. 0.25 mi. upstream of County detention basin F1 Franklin Creek just upstream of entrance into Carpinteria Salt Marsh SM1 Santa Monica Creek just upstream of entrance into Carpinteria Salt Marsh AP1 Arroyo Paredon just below Highway 192 crossing MONT1 Montecito Creek at Val Verde prop., below Hot Springs/Cold Springs confluence MONT2 Montecito Creek just upstream of Hot Springs/Olive Mill Rd. SY1 Sycamore Creek just below Mason St. bridge SY2 Sycamore Creek 300m below Highway 192 crossing and Coyote/Sycamore confluence M1 Mission Creek at De la Guerra St. M2 Old Mission Creek at Bohnet Park M3 Mission Creek at upstream end of Rocky Nook Park M4 Rattlesnake Creek, approx. 0.5 mi. upstream of Las Canovas Rd. crossing M6 Mission Creek, at three falls above Jesuita Trail crossing M7 Old Mission Creek just downstream of Anapamu St. AB1 Arroyo Burro at upstream end of Alan Rd. AB2 Arroyo Burro just downstream of Torino Rd. AB3 San Roque Creek, 0.25 mi. upstream of Foothill Rd. AB4 San Roque Creek just upstream of the confluence with Arroyo Burro AB5 Mesa Creek at entrance to Arroyo Burro estuary AB6 Arroyo Burro just downstream of U.S. 101 AB7 Las Positas Creek just above Veronica Springs Rd. crossing AT1 Atascadero Creek near Patterson Rd. AT2 Atascadero Creek just downstream of Cieneguitas Creek confluence SA1 San Antonio Creek, approx. 0.5 mi. upstream of Tucker's Grove Park SA2 San Antonio Creek, approx. 0.25 mi. upstream of Highway 154 MY1 Maria Ygnacio Creek, approx. 0.25 mi. below San Marcos Rd. crossing

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Table 1: Study Reaches

MY2 Maria Ygnacio Creek, approx. 0.25 mi. upstream of FC detention basin MY3 Maria Ygnacio Creek, approx. 0.25 mi. upstream of Highway 154 SJ1 San Jose Creek, approx. 0.25 mile downstream of U.S. 101 SJ2 San Jose Creek, approx. 0.25 mile upstream of Patterson Rd. crossing SJ3 San Jose Creek at San Marcos Trout Club T1 Tecolote Creek, approx. 50 meters upstream of Vereda del Padre T2 Tecolote Creek, adjacent to Vereda Nueva T3 Tecolote Creek, 100 m downstream from Vereda Parque access DP1 Dos Pueblos Creek, approx. 50 meters downstream of U.S. 101 EC1 El Capitan Creek in State Park, approx. 100 meters upstream of mouth R0 Refugio Creek approximately 0.5 mi. upstream of U.S. 101. R1 Refugio Creek, approx. 1.5 mi. upstream of U.S. 101 R2 Refugio Creek, approx. 0.25 mi. downstream of Circle Barbee Ranch AH1 Arroyo Hondo, approx. 1 mi. upstream of U.S. 101. AH2 Arroyo Hondo, approx. 2 mi. upstream of U.S. 101. SO1 San Onofre Creek, just below U.S. 101 culvert SO2 San Onofre Creek, approx. 1 mi. upstream of U.S. 101 GAV1 Gaviota Creek at State Beach/Park, just below access rd./US 101 junction GAV2 Gaviota Creek, 200 meters downstream of Las Canovas Creek confluence Estuary Study Reaches Ce Carpinteria Creek estuary MONTe Montecito Creek estuary SYe Sycamore Creek estuary Me Mission Creek estuary ABe Arroyo Burro estuary GOLe Goleta Slough estuary BELLe Bell Canyon Creek estuary Te Tecolote Creek estuary GAVe Gaviota Creek estuary Je Jalama Creek estuary

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FIGURE 1: STUDY AREA

Study Area

N Source: Delorme Topoquads

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FIGURE 2: GAVIOTA COAST STUDY REACHES

R2 GAV2 R2 Arroyo San AH2Hondo SO2 Refugio Gaviota Onofre Creek Creek Creek San Arroyo R1 SO2 Onofre Hondo El Creek AH1AH1 Creek R1 Capitan GAV1 Refugio Creek R0 Creek SO1 GAVe EC1 N EC1

Scale: 1 centimeter = 1 kilometer Source: Delorme Topoquads (1999) Study creeks emphasized for ease of recognition

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FIGURE 3: SANTA BARBARA AND GOLETA AREA STUDY REACHES

SJ4 Maria Ygnacio San Jose Creek Creek San SJ3 Antonio MY3 Creek Dos M5 Pueblos Creek MY2 M6 SA2 Tecolote SJ2 MY1 Creek AB3 M4 Sycamore Creek DP1 T2 SA1 T3 SJ1 M3 T1 SY2 Atascadero AB4 SY3 AB6 Mission Creek Te AB7 Creek SY1 Arroyo WINe AT2 Burro AT1 AB2 M2 GOLe M1 SYe AB1 AB5 Me N ABe Scale: 1 centimeter = 1.5 kilometers Source: Delorme Topoquads (1999)

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FIGURE 4: CARPINTERIA AREA STUDY REACHES

Arroyo Paredon Creek

Santa Monica Creek Franklin C3 Rincon AP1 Creek Carpinteria Creek F1 Creek RIN1 SM1 C2 Ce C1 RIN0

N Source: Delorme Topoquads (1999) Study streams emphasized for ease of recognition Scale: 1 centimeter = 2 kilometers

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III. Methods

Physiochemical and biological data for the stream and estuary study reaches was gathered through a combination of methods including field surveys, laboratory analyses, spatial data analyses using geographic information system (GIS) software, and review of United States Geological Survey (USGS) 7.5-minute quadrangle maps and recent aerial photographs. BMI parameters were calculated from the raw data. Statistical tests including linear regressions and analyses of variance (ANOVA) were used to evaluate the streams and estuaries data for relationships with physiochemical parameters and measures of human disturbance, and refine BMI taxa tolerance values and develop the new streams IBI. Further discussion of methods is provided below.

A. Field Surveys 1. Streams Stream surveys involve annual collection of BMI samples and other pertinent physiochemical and biological data at study streams and estuaries using USEPA endorsed rapid bioassessment methodology. Our sampling methodology has been consistent since 2000, and is very similar to that currently used for the California Surface Water Ambient Monitoring Program (SWAMP), the methods of which have varied over the years. As in previous years of the Program, field surveys were conducted in the spring during base stream flow conditions (i.e., low flows). The sampling was conducted in May. Sampling in the spring during base flow conditions provides consistency in the sampling from year to year, as the local stream biota is known to undergo seasonal succession (Cooper et al., 1986). The following was completed during each field survey: • General observations were recorded on a standardized field data sheet, including location, date, time, weather, stream flow conditions, water clarity, and human impacts. • A 100-meter study reach was delineated along the stream. Stream habitat units (i.e., riffles, runs, pools, etc.) within the study reach were mapped and quantified as a percentage of the total reach length. • Stream wetted and channel bottom width were measured at three transects in the study reach. The three transects were established at the 25, 50 and 75 meter marks. Wetted perimeter width is the cross-sectional distance of streambed that is inundated with surface water. Channel bottom width is the cross-sectional distance between the bottoms of the stream banks. • Riparian canopy cover was estimated in the center of the stream channel at the three transects using a spherical densitometer. • Plant and wildlife species observed in the stream and riparian zone were noted and recorded. • Water temperature, conductance, pH, and dissolved oxygen concentration were measured in the field using YSI and Oakton handheld meters. Two measurements of each parameter were made, one in a riffle and the other in a pool, and the two values were averaged.

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• One composite BMI sample was collected from each study reach using a standardized method based on the “multi-habitat” approach described in the USEPA’s Rapid Bioassessment Protocols for Use in Streams and Wadeable Rivers (Barbour et al., 1999). Each sample represents approximately one square meter of stream bottom, collected from 10 individual, 0.1-square meter locations (an approximately 30 cm square). The 10 locations that constituted the sample were selected based on the relative area each stream habitat (i.e., riffles, pools, falls, etc.) covered in the section of stream sampled. For example, if a stream reach contained approximately 50 percent riffles and 50 percent pools, five locations in riffles and five in pools were selected and sampled. Samples were collected using a D-frame net with 500 µm mesh. In locations with flowing water (e.g., riffles and runs), the net was held upright against the stream bottom, and substrata immediately upstream within the 0.1-square meter area was scraped and stirred up for approximately 15 seconds using feet and hands. Dislodged BMIs and stream bottom materials were carried into the net by the stream current. In areas with little or no current (e.g., pools), stream bottom material was stirred up by foot, followed by a quick sweep of the net through the water column to capture dislodged BMIs. This was repeated three times in each pool sampling location. • After each BMI sample was collected, it was rinsed with water in a 500 µm sieve to wash out fine sediments, transferred to a plastic container, and preserved in 70 percent ethanol. • A stream habitat assessment was conducted using the protocol provided in the USEPA’s Rapid Bioassessment Protocols for Use in Streams and Wadeable Rivers. Per this protocol, habitat components were visually assessed and scored, including stream substrate/cover, sediment embeddedness, stream velocity/depth regime, sediment deposition, channel flow status, human alteration, channel sinuosity, habitat complexity/variability, bank stability, vegetative protection, and width and composition of riparian vegetation. Each study reach was assigned a total score of between zero and 200 based on the sum of scores assigned to each habitat component. Criteria from the USEPA protocol were used to guide the scoring. • Quality control measures were incorporated into the field surveys to insure accurate and consistent data gathering. Water monitoring equipment was calibrated regularly. Field crew members have been trained to properly operate equipment, take measurements, collect BMI samples, and conduct stream habitat assessments. Stream habitat assessments were completed by the field crew as a group. 2. Estuaries Ecology conducted a rapid bioassessment survey in each study estuary in early October. Methodology was based on the Tier 1 approach described in Estuarine and Coastal Marine Waters: Bioassessment and Biocriteria Technical Guidance (Bowman et al., 2000). The Tier 1 approach is intended to provide an assessment of coastal wetland habitats based on sampling of one or more biological assemblages (e.g., algae, invertebrates, fish, etc.) and collecting data on water chemistry and bottom characteristics. The following was completed: • General observations were recorded, including study reach location, date, time, weather, water clarity, sediment composition, vegetation, hydrologic condition (i.e., estuary open or closed to ocean), tide conditions, and sources of human disturbance. • Measurements of water temperature, pH, dissolved oxygen concentration, conductance, and salinity were made. When feasible (i.e., Arroyo Burro and Gaviota Creek estuaries),

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measurements were made at 2 monitoring stations in the estuary: one nearest the ocean (i.e., the mouth), and one in the upper (i.e., upstream) portion of the estuary. Measurement sites were spread throughout the estuary to determine if a longitudinal (i.e., downstream to upstream) gradient in salinity or temperature existed due to differential influences of saltwater and freshwater inputs. • BMI samples were collected at the estuary monitoring stations. When the upstream end of the estuary was inaccessible, samples were collected from the downstream end only. Two separate samples were collected at each monitoring station; (1) an infaunal sample consisting of approximately the top 15 cm of sediments from two approximately 10 cm diameter areas of the estuary bottom collected in 0.3 to 0.6 m of water using a core sampler, and (2) an epibenthic sample consisting of material collected in five sweeps with a D-net similar to the pool sampling method for streams (i.e., 0.1 m2 per sweep). After collection, each sample was drained through a 0.5-millimeter mesh sieve to wash out fine sediments, and the remaining material was placed into a plastic bottle filled with 70% ethanol solution for preservation. In total, approximately 0.5 m2 of bottom area was sampled at each monitoring station. • Quality control measures were incorporated into the field surveys to insure accurate and consistent data gathering. Water monitoring equipment was calibrated regularly. Field crew members have been trained to properly operate equipment, take measurements, and collect BMI samples. • A quantitative habitat assessment was developed this year by Ecology and used to rate the habitat quality of each study estuary. Scoring was based on consideration of nine habitat components. Estuary form and perimeter was scored from 0 to 20, while a score from 0 to 10 was given for the other eight components: habitat diversity, connectivity, hydrology, substrate, water column, aquatic vegetation, riparian/upland buffer, and foot traffic/noise/lighting. Scores for each component were added for a total score of 0 to 100. Scoring criteria for each habitat component were carefully developed using our knowledge of local estuaries and the range of conditions present in the study area. Scoring for each estuary was based on field observations and measurements, and review of aerial photography. The estuary habitat assessment sheet is provided as Appendix B. B. Laboratory Analyses BMI samples were processed in the laboratory to determine BMI community composition (i.e., taxa present and relative abundance) and overall density. Each BMI sample was strained through a 500-µm mesh sieve and washed with water to remove ethanol and fine sediments. The sample was placed in a plastic tray marked with equally-sized squares in a grid pattern. The entire sample was spread out evenly across the squares. Squares of material were randomly selected, and sorted one at a time under a dissecting microscope (7X to 50X magnification) until the targeted number of BMIs were located and picked out. The proportion of the sample sorted was noted. For streams, 300 BMIs were picked from each sample for identification. A target of 150 BMIs was set for each estuary sampling site. The infaunal sample was sorted through first, and up to 75 BMIs were picked and identified. Next, the epibenthic sample was sorted, and the remaining number of BMIs were picked and identified to reach the target of 150.

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BMIs were identified with the aid of taxonomic references including Merritt and Cummings (1996) and Smith and Carlton (1975). Insect taxa were identified to the family level. Non- insect taxa (e.g., oligochaetes, crustaceans, etc.) were typically identified to order or class. After sorting and identification, BMIs were bottled in 70 percent ethanol for storage. BMI sample processing methods were clearly established and strictly followed to ensure random selection and accurate enumeration and identification of BMIs. C. GIS Analyses GIS Arcview software was used to calculate upstream watershed area and watershed land use covers for each study reach. Watershed areas were calculated based on watershed boundaries generated in Arcview. Watershed land uses and percent cover for each study reach were calculated by superimposing watershed boundaries over a digital land cover GIS layer for the region. The land cover layer was produced the California Department of Forestry and Fire Protection’s (CDF) Fire and Resource Assessment Program (FRAP). The CDF land use map for the region showed coverage by the following eight land use categories: urban, agriculture, herbaceous, hardwood, shrub, conifer, water, and barren/other. Recent aerial photographs (2013 to 2014) of the region available on Google Earth were reviewed to refine the GIS land use layer. The parameter “% watershed disturbed” was calculated for each study reach by using the following equation: % watershed disturbed = % urban + % agriculture + 0.5(% herbaceous) Herbaceous areas were counted as partially (i.e., half) disturbed to reflect that much of the herbaceous lands in this region are used for livestock grazing or are previously cleared land. D. Review of Topographic Maps USGS 7.5-minute quadrangle topographic maps (1:24,000 scale) for the study area were reviewed to determine stream order, elevation, and gradient for each study reach. Gradient was determined by dividing the elevation change between topographic contours immediately upstream and downstream of the study reach by the stream length between the contours. Stream length was determined by tracing a map wheel over the stream path. E. Study Reach Grouping 1. Streams Stream study reaches were placed into three different groups based on their level of human disturbance. These disturbance groups were assigned to study reaches “a priori” (i.e., before the analyses of biological data) based on physical habitat assessment scores and % watershed disturbed. The following criteria are used to classify study reaches: REF = Stream reaches that are in a “reference condition”, or are minimally to lightly disturbed by human activities. Habitat assessment score is 150/200 or greater, and no more than 5 percent of the upstream watershed is developed with urban or agricultural uses.

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MOD DIST = Stream reaches that are moderately disturbed by human activities. Habitat assessment score is 120/200 or greater, and between 5 and 40 percent of the upstream watershed is developed with urban or agricultural uses. HIGH DIST= Stream reaches that are heavily disturbed by human activities. Habitat assessment score is less than 120 and/or 40 percent or more of the upstream watershed is developed with urban or agricultural uses.

2. Estuaries Estuary study reaches were also placed into three different groups based on their level of human disturbance. These disturbance groups were assigned to study reaches “a priori” (i.e., before the analyses of biological data) based on upstream watershed land use patterns and habitat conditions at the estuary. The following criteria were used to group the study reaches: REF = Estuaries that are minimally to lightly disturbed by human activities. Habitat assessment score is 75/100 or greater, and no more than 10 percent of the watershed area is developed with urban or agricultural uses. MOD DIST = Estuaries that are moderately disturbed by human activities. Habitat assessment score is 50/100 or greater, and between 10 and 40 percent of the watershed area is developed with urban or agricultural uses. HIGH DIST= Estuaries that are highly disturbed by human activities. Habitat assessment score is less than 50/100 and/or greater than 40 percent of the watershed area is developed with urban or agricultural uses.

F. Data Analyses for Streams 1. Calculation of Physiochemical and BMI Metrics Numerous physiochemical parameters and BMI metrics were calculated for each stream study reach using the data collected. Table 2 lists each parameter calculated for the study reaches and the method of calculation (e.g., lab, field, etc.). BMI metrics calculated for each study reach reflect different aspects of community structure, including overall BMI density, richness, composition (i.e., taxa present), the relative and absolute abundances of component taxa or groups, trophic group representation, and sensitivity to human disturbance.

BMI density (number of individuals per m2) was calculated by dividing the number of specimens picked out of the sample by the subsampled area. Richness parameters were determined by counting the number of specified taxa identified in each sample. Functional feeding group parameters (e.g., % collector-gatherers, % scrapers, etc.) were determined using functional feeding group designations for individual taxa provided in Merritt and Cummins (1996).

TV avg., % sens BMIs, and % tol BMIs were calculated using tolerance values for individual BMI taxa ranging from 0 to 10 based on their perceived ability to withstand human disturbance. A tolerance value of 0 indicates that a particular BMI is extremely intolerant of human disturbance, with increasing scores indicating greater tolerance to human disturbance. The methods for determining individual taxa tolerance values is described below under 2. Composite tolerance value averages were calculated by adding the tolerance values for each

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BMI in the sample, and dividing by the total number of individuals. % sens BMIs was calculated by adding the number of BMIs in the sample with a tolerance value of 3 or less, dividing by the total number of individuals in the sample, and multiplying by 100. % tol BMIs was calculated by adding the number of BMIs in the sample with a tolerance value of 7 or greater, dividing by the total number of individuals in the sample, and multiplying by 100. Tolerance values were determined for more than 95 percent of the taxa collected. BMIs without tolerance values were excluded from the calculations of tolerance value averages, % sens BMIs, and % tol BMIs.

Table 2: Physiochemical and BMI Metrics Calculated for Stream Study Reaches Parameters Abbreviation Units Method of Calculation PHYSICAL PARAMETERS Stream order None None USGS Quad Maps Elevation None Feet (ft.) USGS Quad Maps Stream gradient None None USGS Quad Maps Watershed area None Acres GIS % of watershed area disturbed None None GIS Wet stream width None Ft. Field Habitat assessment score None None Field % riparian canopy cover None None Field WATER CHEMISTRY PARAMETERS Stream temperature None °C Field pH None None Field Dissolved oxygen concentration None mg/l Field Specific conductance (corrected to 25° C) None µS/cm Field BMI PARAMETERS BMI density None #/m2 Field/lab # insect families None None Field/lab # Ephemeroptera/Plecoptera/Tricoptera families # EPT families None Field/lab % Ephemeroptera/Plecoptera/Tricoptera % EPT % Field/lab % EPT minus Baetidae % EPT-Baetidae % Field/lab % Plecoptera/Tricoptera % PT % Field/lab % Coleoptera None % Field/lab % Chironomidae None % Field/lab % Diptera None % Field/lab Tolerance value average TV avg. % Field/lab % sensitive BMIs % sens BMIs % Field/lab % tolerant BMIs % tol BMIs % Field/lab % non-insect BMIs None % Field/lab % non-insects + Diptera None % Field/lab % non-insects + Chironomidae None % Field/lab % collector-gatherers % cg % Field/lab % scrapers %sc % Field/lab % shredders %sh % Field/lab % collector-filterers %cf % Field/lab % predators %pred % Field/lab % predators + shredders %pred+sh % Field/lab % scrapers + shredders %sc+sh % Field/lab % scrapers + shredders + predators %sc+sh+pred % Field/lab % collector-gatherers + scrapers + shredders %cg+sc+sh % Field/lab % collector-gatherers + collector-filterers %cg+cf % Field/lab % collector-gatherers + predators %cg+pred % Field/lab

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2. Determination of BMI Tolerance Values for Study Area Streams

Up until 2009, tolerance values for individual BMI taxa published in List of Californian Macroinvertebrate Taxa and Standard Taxonomic Effort (California Department of Fish and Game, 2002) were used to calculate TV avg., % sens BMIs, and % tol BMIs for the study streams. However, by 2009, it became apparent that tolerance values assigned to some of the individual BMI taxa in the List of Californian Macroinvertebrate Taxa and Standard Taxonomic Effort did not agree with the observed distribution of such BMIs in the study area. As an example, the mayfly family Caenidae was assigned a relatively high tolerance value of 7 in the List, yet it was observed in significant numbers only in minimally and moderately disturbed streams in the study area. To address these types of inconsistencies, tolerance values for most BMI taxa specific to the study area were determined in 2009 using the data from Program study reaches. Tolerance values were determined again this year using the same basic methodology employed in 2009. Tolerance values were determined for all BMI taxa having a mean abundance of at least one individual per study reach in at least one of the disturbance groups (REF, MOD DIST, and/or HIGH DIST). For BMI taxa not meeting these criteria, tolerance values from the List of Californian Macroinvertebrate Taxa and Standard Taxonomic Effort were retained. To evaluate their sensitivity to human disturbance, all qualifying BMI taxa were evaluated for differences between the REF, MOD DIST, and HIGH DIST study reach groups using one way analysis of variance (ANOVA). The results of the ANOVAs were used to assign new tolerance values to the qualifying BMI taxa. An ANOVA compares the means and distributions of a given metric among multiple sampling groups, and indicates the probability that the means for the groups are the same. The probability that the means are the same is expressed as p, which is between 0 and 1. The lower the p, the lower the probability that the group means are the same. A p of 0.05 or less is generally accepted as indicating a statistically significant difference between group means. Criteria for setting the new tolerance values are provided in Figure 5. 3. Development of the Updated IBI Developing the updated IBI required the completion of several distinct steps, including: selection of study reaches to be included in the IBI Test Group and those to be included in a separate Validation Group, screening and selection of potential core metrics, defining scoring ranges for potential core metrics, defining IBI scoring categories and ranges, and testing the IBI for accuracy in classifying the biological integrity of individual study reaches. These steps are discussed below. a. Partitioning of Study Reaches into IBI Test Group and Validation Group The IBI Test Group is composed of study reaches surveyed in six or more years. A total of 207 sampling replicates compose the Test Group, including 48 REF, 53 MOD DIST, and 106 HIGH DIST replicates, respectively. Data from these surveys was used to develop the IBI. All study reaches surveyed less than six times over the 15 year Program were included in a separate Validation Group composed of 66 replicates, including 10 REF, 24 MOD DIST, and 32 HIGH DIST replicates, respectively. Study stream reaches in the Validation Group were used to independently test the accuracy of the IBI in correctly scoring and classifying biological integrity.

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Figure 5: Tolerance Values Criteria

Sensitive 0, 1: abundance significantly (p<0.05) highest in REF. MOD DIST (0-3): and HIGH DIST not significantly different from one another. 0 for greater differences in mean values and p between REF and MOD/HIGH DIST, 1 for lesser differences. REF M DIST H DIST 2,3: significant decrease in mean abundance from REF to MOD DIST to HIGH DIST, or from REF and MOD DIST to HIGH DIST. 2 for greater differences in mean values and p, 3 for lesser differences. OR REF M DIST H DIST REF M DIST H DIST

Moderate 4: mean abundance significantly highest in MOD DIST, mean (4-6): abundance in REF significantly higher than in HIGH DIST.

REF M DIST H DIST 5: no significant difference in mean abundance between the three groups. Or mean abundance in MOD DIST sign. higher or lower, and REF and HIGH DIST means not sign. different from each other. OR REF M DIST H DIST REF M DIST H DIST

OR REF M DIST H DIST 6: mean abundance significantly highest in MOD DIST, mean abundance in REF sign. lower than in HIGH DIST.

REF M DIST H DIST

Tolerant 7, 8: significant increase in mean abundance from REF to MOD DIST (7-10): to HIGH DIST, or from REF to MOD DIST and HIGH DIST. 8 for greater differences in mean values and p, 7 for lesser differences. OR REF M DIST H DIST REF M DIST H DIST 9, 10: mean abundance significantly highest in HIGH DIST, REF and MOD DIST not significantly different from each other. 10 for greater differences in mean values and p, 9 for lesser differences.

REF M DIST H DIST

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program Page 27 2014 Report and Updated Index of Biological Integrity Ecology Consultants, Inc. b. Screening of BMI Metrics and Selection of Core Metrics Sensitivity to Human Disturbance To evaluate their sensitivity to human disturbance, all of the BMI metrics calculated were evaluated for differences between the Test Group REF, MOD DIST, and HIGH DIST groups using ANOVA. BMI metrics that most significantly change (i.e., increase or decrease) with increasing levels of human disturbance (i.e., from the REF to MOD DIST to HIGH DIST groups) have the greatest potential to serve as measures of biological integrity and IBI core metrics. Natural Relationships between Potential Core Metrics and Physiochemical Parameters The BMI metrics most sensitive to human disturbance were screened for natural relationships with several physiochemical parameters, which is an important step in determining their suitability for inclusion in the IBI. To illustrate, consider a hypothetical situation where a BMI metric has a significant negative relationship with human disturbance, and also with a physiochemical variable in the absence of human disturbance. If it was also true that the physiochemical parameter was positively influenced by increasing human disturbance, one wouldn’t be able separate the negative effects of increasing human disturbance on the BMI metric from those attributable to natural increases in the physiochemical parameter. This would make the BMI metric unreliable as an indicator of biological integrity. To begin this part of the screening process, multiple regression analyses were performed using the Test Group to evaluate relationships between two human disturbance indicies, % watershed disturbed (landscape level) and habitat assessment score (localized level), and several physiochemical parameters: elevation, gradient, watershed area, stream temperature, specific conductance, and dissolved oxygen concentration. Multiple regression analyses evaluate the relationships of multiple independent variables, or regressors (i.e., % watershed disturbed and habitat assessment score), with that of a single dependent variable, or response variable (i.e., a physiochemical parameter). A best-fit model is calculated that represents the dependent variable as a function of the independent variables. The correlation coefficient (r2) and p-value (p) are calculated in regression analyses, and used to interpret the strength of the relationship between the response variable and the regressors. r2 is given as a value between 0 and 1, and indicates the proportion of the variation in the response variable accounted for by its relationship with the independent variables. The higher the r2, the better the fit of the model. P indicates the probability that the response variable and regressors are not related as predicted by the model, and is given as a value of between 0 and 1. A p of 0.05 or less is generally accepted as indicating a statistically significant relationship between the regressors and response variable. For those physiochemical parameters having significant relationships with the human disturbance regressors, linear regressions were used to evaluate natural relationships between the physiochemical parameters and each of the potential core BMI metrics using data from only the REF study reaches (n=58). Using data solely from the REF study reaches provided an opportunity to evaluate these relationships as they occur naturally, or in the absence of human disturbance. A linear regression calculates a best-fit equation that best represents the relationship between a single independent variable (i.e., the physiochemical variable) and a single response variable (i.e., the BMI metric). r2 and p are calculated similar to the multiple

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Ecology Consultants, Inc. regressions described above, with p of 0.05 or less indicating a statistically significant relationship between the variables. Potential core BMI metrics having no significant natural relationships with any of the physiochemical parameters passed this step of the screening process. Those potential core BMI metrics with significant natural relationships with one or more of the physiochemical parameters required further screening to determine if such natural relationships would confound the interpretation of the relationships between the potential core BMI metric and human disturbance. A confound would arise in one of two scenarios: 1. If the relationship between human disturbance and the physiochemical parameter is positive, and they both affect the BMI metric in the same way (i.e., both positively or both negatively). 2. If the relationship between human disturbance and the physiochemical parameter is negative, and they affect the BMI metric in opposite ways (i.e., one positively and the other negatively). Any BMI metric having one or more such confounding relationship(s) was eliminated from consideration as a core metric in the IBI. Correlations between Potential Core BMI Metrics Remaining potential core BMI metrics were screened to see if they were intercorrelated. Where correlation coefficients were 0.9 or greater, only one BMI metric was retained as a core metric. In such a scenario, the BMI metric having the strongest relationship with human disturbance (per the ANOVA results) was retained as a core metric. Core Metrics The BMI metrics that remained following the above screening processes were retained as core metrics for inclusion in the IBI. To summarize, all core metrics have: 1. A highly significant relationship with human disturbance, either increasing or decreasing between REF to MOD DIST to HIGH DIST groups. 2. No confounding significant natural relationships with physiochemical parameters that impair our ability to interpret the effects of human disturbance on the BMI metric. 3. Correlation coefficients of less than 0.9 with all other core metrics. c. Defining Core Metric Scoring Ranges Scoring ranges were established for each potential core metric on a dimensionless scale of 0 to 10, 0 indicating the lowest level of biological integrity, and 10 indicating the highest level of biological integrity. For metrics that decrease with human disturbance (i.e., highest at REF sites), higher values corresponded with higher scores. For metrics that increase with human disturbance (i.e., highest at HIGH DIST sites), higher values corresponded with lower scores. The distributions of each metric in the REF, MOD DIST, and HIGH DIST groups were used to establish the scoring ranges. Scoring criteria are provided in Table 3.

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Table 3: Core Metric Scoring Range Criteria

Score Scoring Criteria 10 The 75th percentile or greater of the REF group distribution for metrics that are highest in the REF group, or the 25th percentile or lower of the REF group for metrics that are lowest in the REF group 9 The median (50th percentile) to 75th percentile of the REF group for metrics that are highest in the REF group, or the 25th percentile to the median of REF group for metrics that are lowest in the REF group 8 The range between the REF group and MOD DIST group medians is divided and evenly 7 partitioned to provide each scoring range for 6, 7, and 8 6 5 MOD DIST median is the top of the scoring range for 5 4 The range between the MOD DIST group and HIGH DIST group medians is divided and 3 evenly partitioned to provide each scoring range for 5, 4, 3, and 2 2 1 The median to 25th percentile of the HIGH DIST group for metrics that are lowest in the HIGH DIST group, or the median to the 75th percentile of HIGH DIST group for metrics that are highest in the HIGH DIST group 0 The 25th percentile or less of the HIGH DIST group distribution for metrics that are lowest in the HIGH DIST group, or the 75th percentile or higher of the HIGH DIST group for metrics that are highest in the HIGH DIST group d. Calculation of IBI Alternatives and Establishment of IBI Classifications of Biological Integrity Three IBI alternatives were calculated using combinations of the core metrics. The first alternative was calculated by adding all of the core metric scores together. A second IBI alternative was calculated by removing the least sensitive core metric (i.e., with respect to human disturbance), and a third IBI alternative was calculated by removing the two least sensitive core metrics. Based on the distribution of IBI scores for the REF, MOD DIST, and HIGH DIST groups for each IBI alternative, five categories of biological integrity were established: Excellent, Good, Fair, Poor, and Very Poor. Scoring criteria used to establish the categories is provided in Table 4. e. Testing the Accuracy of the IBI Alternatives and Selection of the New IBI

After the IBI was established, the Validation Group (n=66) was used to test the accuracy of the IBI alternatives. IBI scores for each alternative were calculated for the Validation Group study reaches, and classifications of biological integrity were compared to the a priori REF, MOD DIST, and HIGH DIST designations. The accuracy of the IBI alternatives in classifying biological integrity was determined for two and three classes of biological integrity. Table 5 provides criteria for correct classification by the IBI for these two levels of resolution. The percentage of sites properly classified (i.e., accuracy) was calculated for the IBI alternatives using these

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Table 4: IBI Classifications of Biological Integrity and Scoring Criteria

Classification of Biological Integrity Scoring Range Excellent Median of REF group or higher Good From REF group median to 2/3 of way down to MOD DIST group median Fair Upper end of Fair range is MOD DIST group median to 1/3 of way up to REF group median. Lower end of Fair range is MOD DIST group median to 1/3 of way down to HIGH DIST group median. Poor From HIGH DIST group median to 2/3 of way up to MOD DIST group median Very Poor Median of HIGH DIST group or less

Additional statistical analyses were completed to evaluate the relationships between human disturbance and the new IBI, 2009 IBI, and each of the new core metrics using all study reaches as replicates (n=273). This was done to compare the sensitivity of each index and metric to human disturbance. Two types of analyses were completed. First, ANOVAs were completed to compare each index and new core metric for the three study reach groups (REF, MOD DIST, and HIGH DIST). Second, multiple regression analyses were used to evaluate the relationships of each index and core metric with two human disturbance indicies: % upstream watershed undisturbed and habitat assessment score.

Table 5: IBI Accuracy of Classification Criteria

Study Reach Group Accurate to Two Classes Accurate to Three Classes

REF Good to Excellent Fair to Excellent

MOD DIST Top half of Poor to bottom half of Good Poor to Good

HIGH DIST Very Poor to Poor Very Poor to Fair

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4. Relationships Between Average Annual Rainfall vs. Physiochemical and BMI Parameters Other studies have shown that extreme highs (i.e., floods) or lows (droughts) in annual rainfall and corresponding peak stream flows are stressors having major, albeit temporary impacts (typically 1 to 2 years) on stream communities in Meditereanan climates, and in particular in southern California (Cooper et al., 2013, Verkaik et al., 2013.). There have been wide fluctuations in rainfall/stream flow over the course of this study, including some of the driest and wettest years on record. As the IBI is an overall measure of the BMI community of study area streams, it logically follows that extremely high and low rainfall/peak stream flows will temporarily impact IBI scores at affected stream sites, and affect our ability to use the IBI to assess the effect of human disturbances in study area streams. In order to explore the effects of variable rainfall/streamflow on local stream communities, regression analyses were performed to evaluate relationships between average yearly rainfall from 1999-2000 to 2013-2014 and several physiochemical parameters and BMI parameters, including BMI density, abundances of individual taxa, core metrics, and IBI scores using all study reaches as replicates (n=273). Average yearly rainfall was calculated by averaging annual rainfall totals for the wet season (i.e., from September 1 to April 30) from two Santa Barbara County Flood Control District stations: 1. Downtown Santa Barbara (elevation 100 feet), and; 2. San Marcos Pass (2,300 feet elevation). The downtown station has a mean annual rainfall of 17.5” in over 130 years of records, with a high of 45” in the 1997-1998 rainy season. The San Marcos Pass station has a mean annual rainfall of 35” in 47 years of records, and a high of 88” in 1982-1983. ANOVAs were used to evaluate differences in IBI score among three average annual rainfall categories: Wet (>30 inches), Moderate (15.01-30 inches) and Dry (≤15 inches). ANOVAs were also completed to evaluate differences in mean IBI scores among REF study reaches in individual years (i.e., 2000, 2001, and so on to 2014). It was postulated that the true relationship between IBI score and rainfall could be seen among the REF group, without potentially overwhelming impacts from human disturbance in the HIGH DIST and possibly MOD DIST groups. Finally, ANOVAs were completed to compare mean IBI score between disturbance groups for each individual year (i.e., 2000, 2001, and so on to 2014). This was done to evaluate the IBI’s performance in differentiating between the disturbance groups in each year despite background effects of variable rainfall and streamflow. 5. Analyses of Wildfire Impacts on Local Streams Wildfires are another type of episodic disturbance that other studies have shown to have major, albeit temporary impacts (typically 1 to 2 years) on stream communities in Meditereanan climates, and in particular in southern California (Cooper et al., 2013, Verkaik et al., 2013.). Four major wildfires have occurred in the study area since 2000: Gaviota (June, 2004), Gap (July, 2008), Tea (November 2008), and Jesusita (May 2009). The watersheds of several stream study reaches were burned to varying extents (4 to 80 percent) by these fires. As an example, Plate 3 shows the boundaries of the Jesusita Fire in relation to the study streams and watersheds it affected.

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Plate 3: Jesusita Fire Map (source: County of Santa Barbara, 2009)

note: fire perimeter is the solid black line

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Two-way ANOVAs were used to examine the effects of the fires on study streams by comparing riparian canopy cover, stream temperature, habitat assessment score, and IBI score for the year before (year 0) and years 1 to 5 after each fire in study reaches in burned vs. unburned watersheds. Study reaches included in the analyses were those in burned and unburned basins where sampling occurred in a pre-fire year and at least one year within the 5 years after fire. Because fire effects on local stream BMI communities depend critically on characteristics of the fire (extent, severity, distribution), watersheds (gradient, soils), subsequent rainfall events (magnitude, intensity, timing, frequency), and time since fire (Verkaik et al. 2013), we attempted to disentangle some of the effects of these variables on BMI responses to fire. We assumed that the extent of fire would alter both erosion rates and riparian vegetation and that gradients would affect erosion rates with collective impacts on habitat assessment scores (particularly because of the deposition of fine sediment) and riparian canopy cover which, in turn, would affect BMI communities (measured as IBI scores). We also assumed that fire impacts would attenuate with increasing time since or distance from fires. As a consequence, we performed multiple regression analysis on only burned sites at years 1 through 5 after fire using riparian canopy cover, stream temperature, habitat assessment score, and IBI score as dependent variables and fire extent (% of drainage basin burned), gradient, cumulative rainfall before sampling, and downstream distance from the fire’s lower perimeter as the independent variables. 6. Analyses of Effects of Stream Habitat Restoration Efforts Significant habitat restoration efforts have been made at stream sites M2 (old Mission Creek) and AB5 (Mesa Creek). In the case of M2, restoration involved bank stabilization, bioswale construction, UV water treatment (i.e., to kill bacteria), and native riparian replanting along approximately 150 meters of stream channel. Restoration work at AB5 involved daylighting an underground storm drain, creating a creek channel and planting it with native riparian vegetation.

Regression analyses were completed to evaluate differences in Habitat Assessment (HA) and IBI values between AB5 (restored) and AB1 (control), and also between M2 (restored) and M1 (control), through time after restoration. The regressions were completed to determine whether measurable improvements in habitat quality and BMI communities of M2 and AB5 occurred through time compared to a control site. In the case of M2, bioassessments were completed for three years prior to restoration activities. The presence of this data allowed for the completion of a before-after-control-impact (BACI) analysis of M2 (restored) versus M1 (control). The BACI used ANOVA to compare the differences between HA and IBI values at M2 and M1 before and after the restoration. A BACI analysis was not possible for AB5, as no bioassessments were conducted prior to restoration (i.e., the stream was an underground pipe).

G. Data Analyses for Estuaries 1. Calculation of Physiochemical and BMI Metrics Numerous physiochemical parameters and BMI metrics were calculated for each study estuary using the data collected. Table 6 lists each parameter calculated for the study reaches and the method of calculation (e.g., lab, field, etc.). 13 BMI metrics were calculated for the study

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Table 6 Physiochemical and BMI Metrics Calculated for Study Estuaries

Units of Method of Parameters Abbreviation Measurement Calculation PHYSICAL PARAMETERS Watershed area None Acres GIS Percent of watershed area disturbed None % GIS/aerial photos Habitat assessment score None % Field/aerial photos Width None Feet Field/aerial photos Length None Feet Field/aerial photos Surface area None Acres Field/aerial photos Depth None Feet Field Buffer vegetation width None Meters Field/aerial photos % native buffer vegetation None % Field Depth None Feet Field/aerial photos WATER CHEMISTRY PARAMETERS Water temperature None Degrees celsius (°C) Field pH None None Field None Milligrams per liter Dissolved oxygen concentration Field (mg/l) Specific conductance (corrected to 25° None µS/cm Field Celsius) None Parts per thousand Salinity Field (ppt) BIOLOGICAL PARAMETERS BMI density None # per m2 Field/lab # of taxa # taxa None Field/lab # of sensitive taxa # sens taxa None Field/lab # of tolerant taxa # tol taxa None Field/lab # sensitive taxa/# tolerant taxa # sens/ # tol None Field/lab % sensitive BMIs % sens BMIs % Lab % tolerant BMIs % tol BMIs % Lab % insects None % Lab % non-insects None % Lab % dominant taxon None % Lab % 2 dominant taxa None % Lab % predators % pred % Lab % collector-gatherers % cg % Lab

BMI density (number of individuals per m2) was calculated by dividing the number of specimens picked out of the sample by the subsampled area. Richness parameters were determined by counting the number of specified taxa identified in each sample. % sensitive BMIs, and % tolerant BMIs were calculated by adding the number of BMIs in the sample labeled as either “sensitive” or “tolerant” to human disturbance, dividing by the total number of individuals in the sample, and multiplying by 100. # sensitive taxa and # tolerant taxa were calculated by adding

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Ecology Consultants, Inc. the number of taxa with these labels. Taxa have been labeled as being “sensitive” or “tolerant” to human disturbance, or neither (i.e., moderate) using methods described below. Functional feeding group parameters (e.g., percent collector-gatherers, % predators) were determined using functional feeding group designations for individual taxa provided in Merritt and Cummins (1996). % dominant taxon and % 2 dominant taxa were determined as the percentage of the sample represented by the most common and two most common taxa, respectively. 2. Establishing the Sensitivity/Tolerance of Individual BMI Taxa to Human Disturbance ANOVAs were completed to compare mean abundances of individual BMI taxa among the REF, MOD DIST, and HIGH DIST groups. This was done to evaluate disturbance sensitivity of the individual taxa, and identify taxa that could be useful in developing BMI community metrics (i.e., % sensitive BMIs and % tolerant BMIs) that may serve as reliable indicators of biological integrity. Individual taxa evaluated with ANOVA had a mean abundance of at least 0.5 individuals per site in at least one of the disturbance groups. Taxa with higher mean abundance at REF sites compared to HIGH DIST sites with significant or near significant results were labeled at “sensitive”. Taxa with higher mean abundance at HIGH DIST sites compared to REF sites with significant or near significant results were labeled as “tolerant”. Taxa that did not meet either of these criteria were considered to have moderate tolerance to human disturbance. 3. Establishing the Sensitivity/Tolerance of BMI Metrics to Human Disturbance ANOVAs were completed to compare mean values for 13 BMI metrics among the REF, MOD DIST, and HIGH DIST groups to evaluate their disturbance sensitivity. BMI metrics with significant differences in means between REF and HIGH DIST groups were considered sensitive to human disturbance, and candidates as core metrics for a future estuarine IBI. 4. Salinity Effects Linear regressions were completed to explore the natural relationships of salinity and the potential indicator BMI metrics in REF estuaries. REF estuaries only were used in these analyses to screen out potentially confounding influences of human disturbance. Understanding the influences of natural physiochemical variability will be an important part of the process of screening potential BMI indicator metrics. Salinity is expected to be the most important natural physiochemical factor affecting BMI composition in local estuaries. Other physiochemical parameters will be considered in the future as the REF sites data set grows.

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IV. Results and Discussion A. Physiochemical and Biological Data Table A-1 in the Appendix provides physiochemical data collected at the streams study reaches for all years (2000-2014). Table A-1 also lists BMI taxa and abundances for each stream study reach, as well as calculated BMI metrics and IBI scores. New tolerance values, as well as functional feeding groups, are provided for individual BMI taxa. Discussions of the BMI metrics, IBI scores, and BMI tolerance values are provided later in this section. Table A-2 provides a list of the plant species observed at each stream study reach surveyed this year, and the number and percentage of native vs. introduced plant species observed. Table A-3 provides a list of vertebrate species observed at the stream study reaches. For study reaches that have been surveyed multiple times, plant and vertebrate species observations are combined over all surveyed years. Table A-4 provides physiochemical and BMI data and metrics for the study estuaries for 2012-2014.

B. Streams Data Analyses 1. BMI Tolerance Values

Tolerance values and sensitivity designations for individual BMI taxa were determined using ANOVAs as described in Methods. Table A-5 in the Appendix summarizes the results of the ANOVAs, and provides tolerance values (new and previous) for the individual taxa. Figure 6 illustrates the ANOVA results for three taxa: Heptageniidae (sensitive), Baetidae (moderate), and Chironomidae (tolerant). Overall, there was close agreement with the 2009 analyses; tolerance values were unchanged for 69 of the 72 BMI taxa with established tolerance values. The three taxa with changes in tolerance values were as follows: Sialidae 3 to 4 Gastropoda 5 to 7 Isopoda 8 to 9

Per the minimum mean abundance of at least one individual per study reach in at least one of the disturbance groups, tolerance values were determined using ANOVAs for 46 of the 80 BMI taxa found in the study area (see Table A-5). Sensitive taxa (tolerance values of 0 to 3) determined by the ANOVAs included most of the EPT taxa (i.e., mayflies, stoneflies, and caddisflies), two Coleoptera (Elmidae and Psphenidae), two Dipterans (Tipulidae and Stratiomyidae), the Hemipteran Veliidae, three Odonates (Aeshidae, Gomphidae, and Cordulegastridae), and Acari (water mites). A few EPT taxa including Baetidae (mayfly), Hydropsychidae, Hydroptilidae, and Philoptomatidae (caddisflies) had moderate disturbance tolerance (tolerance values of 4 to 6), either showing no differences in mean abundance between disturbance groups, or significantly highest abundance in the MOD DIST group. Other moderately tolerant taxa included the Coelopteran Dystidae, Dipterans Ceratopogonidae and Psychodidae, Hemipteran Naucoridae, Odonates Coenagrionidae and Lestidae, the Megalopteran Sialidae, and Amphipoda. Tolerant taxa (tolerance values of 7 to 10) included Coelopteran Halipidae, Dipteran Chironomidae and Simulidae, and several non-insects (Gastropoda, Ostracoda, Cladocera, Copepoda, Isopoda, and Oligochaeta).

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Figure 6: Examples of Tolerance Value Determinations through ANOVA of Individual BMI Taxa at REF, MOD DIST, and HIGH DIST Reaches

Means and distributions of Heptageniidae, Baetidae, and Chironomidae abundance (# of individuals per sample) for disrubance groups REF, MOD DIST, and HIGH DIST are shown. Heptageniidae is disturbance sensitive (TV=0), Baetidae has intermediate sensitivity (TV=5), and Chironomidae is disturbance tolerant (TV=8). Top and bottom of diamonds are the 95 percent confidence limits, and the centerlines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles. The p value is for the ANOVA where abundance is the dependent variable and disturbance category is the independent variable. R2 is the proportion of variation in the dependent variables accounted for by the disturbance categories.

N=207, p<0.0001, r2 = 0.41

N=207, p=0.9027, r2 = 0.001

N=207, p<0.0001, r2 = 0.14

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Tolerance values were available in CDFG (2002) for 26 of the 34 remaining taxa (see Table A- 5). There were 8 BMI taxa found in the study reaches without tolerance values, as they did not meet the minimum criteria for establishment of tolerance values in this study, nor do they have tolerance values in CDFG (2002). These are Chrysomelidae, Hydraenidae, Notonectidae, Lepidoptera, Hymenoptera, Nematomorpha, Nematoda, and Bivalvia. Individuals from these taxa were not included in the calculations of TV avg., % sens BMIs, and % tol BMIs. 2. Development of the Updated IBI a. Screening and Selection of Potential Core Metrics Sensitivity to Human Disturbance Table A-6 summarizes the results of the ANOVAs conducted to evaluate the relationships of the BMI metrics to human disturbance. As an example, Figure 7 illustrates the ANOVAS for # EPT families, which had a highly significant negative relationship with human disturbance, and TV avg., which had a highly significant positive relationship with human disturbance. Overall, 22 of the 26 BMI metrics evaluated had significant differences among the REF, MOD DIST, and HIGH DIST groups, including 20 with p<0.0001. BMI metrics with the strongest negative responses to human disturbance were # EPT families (p<0.0001, r2=0.65), % sensitive BMIs (p<0.0001, r2=0.60), % EPT-Baetidae (p<0.0001, r2=0.57), # insect families (p<0.0001, r2=0.54), % sh+pred (p<0.0001, r2=0.45), and % PT (p<0.0001, r2=0.45). BMI metrics with the strongest positive responses to human disturbance were TV avg. (p<0.0001, r2=0.59), and % tolerant BMIs (p<0.0001, r2=0.42). These eight metrics were all considered for further analyses as potential core metrics. The only metrics evaluated that did not show significant differences among study reach groups were percent scrapers, BMI density, percent collector-gatherers and percent collector-gatherers + collector-filterers. Natural Relationships between Potential Core Metrics and Physiochemical Parameters Table A-7 summarizes the results of the multiple regression analyses conducted using the Test Group (n=207) to evaluate relationships between the disturbance regressors (% watershed disturbed and habitat assessment score) and the physiochemical parameters elevation, gradient, watershed area, stream temperature, specific conductance, and dissolved oxygen. With the exception of dissolved oxygen, all of the physiochemical parameters were significantly related to the disturbance regressors at p<0.0001, and were used in the ensuing linear regressions.

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Figure 7: ANOVA Comparisons of # EPT families and TV avg. at REF, MOD DIST, and HIGH DIST Reaches Means and distributions of # EPT families and TV avg. for disturbance groups are shown. Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles. The p value is for the ANOVA where # EPT families/TV avg. are the dependent variables and disturbance category is the independent variable. R2 is the proportion of variation in the dependent variables accounted for by the disturbance categories.

N=207, p<0.0001, r2 = 0.65

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Table A-8 summarizes the results of the linear regressions conducted to evaluate natural relationships between each of the eight potential core metrics and physiochemical regressors across the REF study reaches (n=58). Most of the potential core metrics had significant natural relationships with one or more physiochemical parameters across the REF sites, but these relationships were much weaker compared to those between the potential core metrics and human disturbance, as evidenced by lower r-square and higher p. Table A-8 also provides a breakdown of each significant relationship between the potential core metrics, physiochemical parameters, and human disturbance, and the direction of the relationships (i.e., positive or negative). Based on the direction of the relationships and the logic described in the Methods, conclusions about confounds introduced by relationships among biotic, physicochemical, and land disturbance metrics are derived.

As indicated in Table A-8, none of the significant natural relationships between the potential core metrics and physiochemical parameters across REF sites confounded the interpretation of relationships between potential core metrics and human disturbance. Therefore, none of the potential core metrics were eliminated based on their natural relationships with physiochemical parameters. To provide an example, consider the potential core metric #EPT families, which had a significant positive natural relationship with watershed area. Watershed area and human disturbance also have a positive relationship. If #EPT families was positively related to human disturbance, one wouldn’t be able to separate natural positive effects of increasing watershed area from those of increasing human disturbance, and a confound would exist in interpreting the relationship between #EPT families and human disturbance. However, #EPT families and human disturbance were negatively related, so there was no confound. Correlations between Potential Core BMI Metrics Table A-9 presents the results of the correlation analyses between the potential core metrics. There were two metrics correlated at 0.9 or greater: % sens BMIs and %EPT-Baetidae (0.93). % sens BMIs has a stronger relationship with human disturbance and thus was retained as a core metric, while % EPT-Baetidae was eliminated. Core Metric Selection Based on the results presented above, seven core metrics were selected for inclusion in the IBI. These are listed below in order of their strength as indicators of biological integrity, as determined by the strength of their relationships with indicies of human disturbance. • # EPT families • % sens BMIs • TV avg. • # insect families • % sh+pred • %PT • % tol BMIs

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Six of the seven core metrics were part of the 2009 IBI. The new core metric is % tol BMIs. % EPT-Baetidae, which was in the previous IBI, was eliminated due to its high correlation with % sens BMIs. The core metrics selected were those most sensitive to human disturbance with no confounding natural relationships with physiochemical parameters. Collectively, the core metrics are diversified in that they represent different aspects of community structure including taxa richness, composition, disturbance sensitivity, and trophic structure. b. Defining Scoring Categories and Ranges for Core Metrics Scoring ranges were developed for the core metrics using the criteria presented in Methods. The scoring ranges are provided below in Table 7.

Table 7: Core Metric Scoring Ranges # EPT % sens # insect % shredders TV Avg. %PT % tol BMIs Score families BMIs families +predators 10 ≥15 ≥58 ≤3.62 ≥ 28 ≥ 25 ≥ 20 ≤ 16 9 14 44 to 57 3.63 to 4.40 26, 27 18 to 24 15 to 19 17 to 27 8 13 37 to 43 4.41 to 4.79 23 to 25 16, 17 13, 14 28 to 32 7 11, 12 29 to 36 4.80 to 5.18 21, 22 14, 15 10 to 12 33 to 37 6 9, 10 21 to 28 5.19 to 5.56 19, 20 12, 13 7 to 9 38 to 42 5 7, 8 17 to 20 5.57 to 5.91 17, 18 10, 11 5, 6 43 to 49 4 5, 6 12 to 16 5.92 to 6.26 15, 16 8, 9 4 50 to 57 3 4 7 to 11 6.27 to 6.60 13, 14 6, 7 3 58 to 65 2 3 2 to 6 6.61 to 6.93 11, 12 4, 5 2 66 to 73 1 2 1 6.94 to 7.53 6 to 10 3, 4 1 74 to 90 0 0, 1 0 ≥7.54 ≤ 5 ≤ 1 0 ≥ 91 c. IBI Alternatives and Classifications of Biological Integrity The score ranges for the three IBI alternatives across the five categories of biological integrity are provided in Table 8. Alternative 1 is made up of the five strongest core metrics, Alternative 2 is made up of the six strongest core metrics, and Alternative 3 is made up of all seven core metrics.

Table 8: IBI Alternatives and Classifications of Biological Integrity

Classification of Scoring Range Biological Integrity Alternative 1 Alternative 2 Alternative 3 (5 core metrics) (6 core metrics) (7 core metrics) Excellent 44 to 50 51 to 60 59 to 70 Good 33 to 43 40 to 50 46 to 58 Fair 20 to 32 25 to 39 29 to 45 Poor 7 to 19 8 to 24 11 to 28 Very Poor 0 to 6 0 to 7 0 to 10

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Table 9: Accuracy of IBI Alternatives

IBI Alternative Accuracy to 2 Classes of Accuracy to 3 Classes Biological Integrity of Biological Integrity

Alternative 1 (top 5 core metrics) 82% 95%

Alternative 2 (top 6 core metrics) 82% 95%

Alternative 3 (all 7 core metrics) 86% 98%

As shown in the table, Alternative 3 had the greatest accuracy in properly classifying sites from the Validation Group. The accuracy level of Alternative 3 was 86% to two classes of biological integrity, and 98% to three classes of biological integrity, respectively. As such, Alternative 3, comprised of all seven core metrics, was selected as the updated IBI. Updated IBI scores for all study reaches (n=273) are provided in Table A-1. As described in Methods, ANOVAs were completed to evaluate the relationships between human disturbance and the updated IBI, 2009 IBI, and each of the new core metrics using all study reaches as replicates (n=273). ANOVA results are summarized in Table A-10, and illustrated in Figure 8. Multiple regression analyses were completed to evaluate the overall relationships between the updated IBI and 2009 IBI versus two human disturbance regressors (% watershed undisturbed and habitat assessment score). Figure 9 illustrates and summarizes the results of the regressions. The updated IBI and 2009 IBI have strong relationships with indicies of human disturbance. The ANOVA results show similar sensitivity to human disturbance for the updated IBI (p<0.0001, r2=0.62) compared to the 2009 IBI (p<0.0001, r2=0.62). The results of the multiple regression analyses are similar, with the new IBI (p<0.0001, r2=0.65) having slightly higher r2 compared to the 2009 IBI (p<0.0001, r2=0.63). Each of the new core metrics were significantly related to indicies of human disturbance (see Table A-10). Human disturbance could not account for as much of the variation in values for these metrics as for variation in IBI values.

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Figure 8: ANOVA Comparison of Updated IBI Score at REF, MOD DIST, and HIGH DIST Reaches

Means and distributions of updated IBI score for study reach groups are shown (p<0.0001, r2 = 0.65). All study reaches were used as replicates (n=273). Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles.

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Figure 9: Multiple Regression Analyses of Updated IBI Score vs. Human Disturbance Regressors

The graphs below illustrate the relationship between updated IBI score (dependent variable, y- axis) and the human disturbance regressors % watershed undisturbed and habitat assessment score (independent variables, x-axis). The best-fit models are shown as the solid red lines. The dotted red lines are the error bars for the slope of the model (i.e., at p=0.05 confidence limits) All study reaches were used as replicates (n=273). The top graph is for the whole model, and shows the actual data plotted against what is predicted for each replicate by the best-fit model (r2=0.65, p<0.0001). The bottom graphs show the leverage plots of updated IBI score vs. the individual regressors.

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3. Relationships between Average Annual Rainfall vs. Physiochemical and BMI Parameters Table A-11 in the Appendix summarizes the results of the linear regression analyses of selected physiochemical and BMI parameters vs. annual average rainfall. There were significant positive relationships between average annual rainfall and wet width (p<0.0001, r2 = 0.07) and dissolved oxygen (p<0.0001, r2 = 0.10). There was a significant negative relationship between rainfall and specific conductance (p=0.0049, r2 = 0.03). These relationships are intuitive, as higher stream flows in wetter years should result in wider channels carrying more oxygenated, more diluted water (i.e., less groundwater influence), and vice versa in drier years. The low r2 indicate that rainfall could explain only very small amounts of the variation in the response variables. There were no significant relationships between rainfall and habitat assessment score, stream temperature, or riparian canopy cover. The linear regressions show significant negative relationships between rainfall and % sens BMIs (p=0.0011, r2 = 0.04), %sh+pred (p=0.0035, r2 = 0.03), %PT (p=0.0242, r2 = 0.02), and % tol BMIs (p=0.0017, r2 = 0.04). The low r2 indicate that rainfall could explain only very small amounts of the variation in these response variables. There were not significant relationships between rainfall and the following core metrics: #EPT families, TV avg., and # insect families. There was a significant negative relationship between rainfall and BMI density (p=0.0017, r2 = 0.04). There was a strong significant positive relationship between rainfall and the abundances of Baetidae (p<0.0001, r2 = 0.40) and Simuliidae (p<0.0004, r2 = 0.05). There were significant negative relationships between rainfall and the abundances of the mayfly families Caenidae (p<0.0001, r2 = 0.07) and Leptohyphidae (p<0.0001, r2 = 0.07), Gastropoda (p<0.0001, r2 = 0.07), and Ostracoda (p<0.0001, r2 = 0.14). There was no relationship between rainfall and the Chironomidae, the most ubiquitous and abundant taxa in in the study streams. 4. Relationship between IBI Score and Average Annual Rainfall The linear regression showed no discernable relationship between IBI score and average annual rainfall (p=0.2692, r2 = 0.005). The results of the ANOVA of IBI score by the Wet, Moderate, and Dry rainfall groups (see Figure 10) showed that the moderate rainfall group had the highest mean IBI score (32), followed by Dry (28) and Wet (25). While the differences in means were not statistically significant (p=0.1547, r2 = 0.01), these results provide evidence that low and high extremes in rainfall have mild negative impacts on IBI score. The results of the ANOVA of IBI score year to year for the REF group (n=56) are summarized in Table A-12. Figure 11 illustrates the ANOVA. Using only REF sites eliminated any potentially confounding influences of human disturbance on IBI scores, allowing the relationship between IBI scores and rainfall to be more clearly examined. The REF group had significantly lower IBI scores for two of the years compared to most of the other years: 1. 2005, which had a mean IBI score of 37 and was the second highest rainfall year in over 130 years of records, and: 2. 2014, which had a mean IBI score of 33, and was the 3rd year in a row of severe drought, and one of the lowest rainfall years on record.

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Figure 10: ANOVA Comparison of IBI Score for Wet, Moderate, and Dry Rainfall Groups

Means and distributions of new IBI score for the rainfall groups are represented (p=0.1547, r2 = 0.01). All study reaches were used as replicates (n=273). Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles.

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Figure 11: ANOVA Comparison of IBI Score by Year for REF Streams

Means and distributions of IBI score by year for each of the three disturbance groups are represented below. Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 and 75 percent quantiles. 2005 and 2014 have significantly lower mean IBI score compared to most other years, no other significant differences amongst years (p=0.0003, r2 = 0.55, n=56).

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There were not any other significant differences in mean IBI score among years for the REF streams. The remaining years had average IBI scores ranging from 49 to 68. Based on the above, IBI scores appear to be naturally lower immediately following extremely high rainfall years, and after periods of prolonged drought, compared to more moderate rainfall years. This makes sense, as: • High rainfall years produce high stream discharges that scour and wash out large quantities of streambed material and BMIs in some sections, and bury them in others. The following spring, the BMI community is in a state of recovery, as evidenced by lower overall BMI density, lower relative abundances of many taxa such as pool dwelling Caenidae and Leptohyphidae, Ostracoda, and Gastropoda, and higher relative abundances of early colonizers including Baetidae and Simulidae. • Periods of prolonged drought (such as 2012 to 2014) result in very low stream flows or dry conditions, reducing or eliminating aquatic habitat. In stream sections that dry up, BMIs are lost, and the community has to start over when stream flows return via colonization from remaining wet reaches of the stream or other watersheds (e.g., by aerial insects). • Moderate rainfall years typically create more stable and sustained flows, which create the conditions for a more balanced and mature BMI community. The ANOVAs comparing IBI score by disturbance group for each year from 2000 to 2014 showed significant differences amongst the groups in mean IBI score in all 15 years of study. Table A-13 summarizes the results, and Figure 12 illustrates the ANOVAs for selected years. Mean IBI score increased from HIGH DIST to MOD DIST to REF in all years. This includes 2005, of the extreme high rainfall year, and 2014, which followed three consecutive years of drought. MOD DIST and REF scores were depressed in 2005 and 2014, but the IBI still differentiated appropriately between each disturbance group. To summarize the above analyses, the local BMI community as a whole has remained fairly stable except following: 1. Extremely high rainfall years, and: 2. Periods of prolonged drought where stream flows become extremely low or absent. This is reflected by the IBI, which has been designed to measure the integrity of the BMI community. While IBI scores have been naturally lower in magnitude and range in extreme rain years, the IBI has still properly differentiated between REF, MOD DIST, and HIGH DIST groups at a significant level for each of the 15 years of the Program. This is despite the fact that statistical power has been lower the last few years, as fewer stream reaches have been surveyed to allow for the study of estuaries.

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Figure 12: ANOVAs of IBI Score for HIGH DIST, MOD DIST, and REF Disturbance Groups for Selected Years

Means and distributions of IBI score for each of the three disturbance groups for selected years (2005 and 2009) are shown below. Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles.

2005 (p=0.0003, r2 = 0.64, n=19)

2009 (p<0.0001, r2 = 0.86, n=24)

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5. Wildfire Impacts on Local Streams

Table A-14 lists the study reaches included in the ANOVA analyses of burned vs. unburned streams, and criteria used to select burned and unburned sites. Table A-15 summarizes the results of the ANOVAs, while Figure 13 illustrates IBI and habitat assessment scores by year, disturbance category, and fire category (i.e., burned or unburned). Habitat assessment scores and IBI scores were significantly higher at unburned than burned sites for the first year after fires, and IBI scores additionally were significantly higher at unburned than burned sites in the second year after fire. Further, there was a significant fire X human disturbance effect on IBI values four years after fire, when IBI values were higher at burned than unburned sites for the HIGH DIST category and where they showed the reverse pattern at MOD DIST sites. The IBI trajectories suggest that fire had negative effects at REF sites in the first post-fire year and at MOD DIST sites in the 2nd post-fire year, but that fire may have benefited HIGH DIST sites by the 4th post-fire year, perhaps owing to increased flow and scour (Coombs and Melack 2013). Temperatures were higher at burned than unburned sites after 5 post-fire years. Taxa associated with streams in burned (Baetidae, Simulidae) basins were similar to those associated with streams indicative of wet years, suggesting that the responses of invertebrate communities to both fire and floods were similar. Taxa typical of unburned sites included those associated with REF sites (Heptageniidae, Leptophlebidae) or dry years (Ostracoda, Gastropoda). Table A-16 summarizes the results of the multiple regression analyses of the response variables (IBI score, habitat assessment score, stream temperature, and riparian canopy cover) vs. fire extent, distance from fire, and the other independent variables. Fire extent was not related to site elevation, drainage area, gradient, or downstream distance from the fire, but downstream distance from the fire was related to all of the topographic variables (r’s = -0.52 with elevation, -0.55 with gradient, +0.47 with drainage area, all p’s < 0.05). As expected, gradients were higher, and distances from fire lower, for REF and MOD DIST sites than HIGH DIST sites (p < 0.05, Tukey’s HSD tests). In the first year after fire, but not subsequent years, temperature increased (p < 0.01) and IBI values decreased (p < 0.01) with increasing fire extent. Habitat assessment scores were negatively related to fire extent in the 3rd post-fire year. Downstream distance from the fire was positively related to temperature in post-fire years 1–4 and negatively related to IBI scores in years 1 and 3 and to habitat assessment scores in post-fire year 3, but these relationships reflected general downstream increases in temperature and declines in IBI scores and habitat assessment scores associated with human disturbance, rather than downstream changes in fire impacts. Fire apparently had little immediate effect on riparian canopy cover, indicating the fires did not burn riparian vegetation at the study sites. In summary, IBI scores were significantly higher at unburned than burned sites for the first two years after fire. Habitat assessment scores were significantly lower at burned than unburned sites for the first post fire year. Fire extent (i.e., percentage of watershed burned) had a significant negative relationship with IBI score and a significant positive relationship with stream temperature in the first post fire year, and a significant negative relationship with habitat assessment score in the 3rd post fire year. The influence of distance from fire on the response variables was confounded by human development patterns (i.e., study reaches further from fires were further downstream in more developed areas). Overall, most effects of fire on BMI communities (and other response variables) were observed for only one to two years after fire

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Figure 13: IBI and Habitat Assessment Scores by Year, Disturbance and Fire Category

Average habitat assessment scores and IBI scores for the year before (0) and years 1 – 5 after fires for sites in different human disturbance (Ref, Mod, High) X fire categories (i.e., burned-B or unburned-U). Two-way analysis of variance including habitat and IBI scores as dependent variables and human disturbance category and burned status (unburned vs. burned) as independent variables (and their interaction) showed significant effects of human disturbance on habitat and IBI score across all times and significant main effects of fire on habitat score in post-fire year 1 (p < 0.05) and on IBI score in post-fire years 1 and 2 (p’s < 0.05 and 0.01). The only significant fire X disturbance category interaction effect was observed for the IBI score in post-fire year 4 when IBI scores were higher at burned than unburned sites in the highly disturbed category and the reverse being observed at moderately disturbed sites. See Tables A-14 and A-15 for more details on the ANOVA categories and results.

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6. Stream Habitat Restoration Sites The analyses of habitat restoration sites M2 and AB5 indicate that restoration activities were effective in improving habitat quality, as measured by habitat assessment (HA) score. The BACI analysis showed that the difference in HA scores between control and restored Mission Creek sites were significantly lower in the pre vs. post-treatment years (ANOVA, F1,9, p < 0.02) (see Figure 14). In general, HA scores were lower at the M2 than M1 site before restoration, but were consistently higher in the period after restoration. HA scores were much lower at the restored AB5 site than at the control AB1 site in the first two years after restoration, but improved to levels found in the control site after three years. The relationship between HA score differences between the AB5 and AB1 sites and sampling year was marginally significant and positive (see Figure 15). Improvement in HA scores at M2 and AB5 owes largely to dramatic improvements in streamside, riparian vegetation that have resulted from restoration efforts. Native riparian plant cover is vastly improved at these sites, as is riparian canopy cover, which has increased from 68 percent at M2 pre-restoration to 95 percent in 2014, and from 45 percent at AB5 following initial restoration to 100 percent in 2014. The vastly improved riparian habitat at M2 and AB5 has improved bank stability, and also lowered stream temperature, which has consistently been below 20° C at both sites for many years. Dissolved oxygen has been 6 mg/l or greater for many years at both sites. Although restoration activities have improved habitat quality, this improvement was not reflected in IBI scores. The BACI analysis showed no difference between control and restored IBI differences in Mission Creek for pre versus post-restoration times (ANOVA, F1,9 = 0.1, p > 0.70) and the regression analyses showed no temporal trend in the differences in IBI values 2 between control and restored sites (M2 – M1 IBI values, overall regression: F1,9 = 0.06, R = 0, 2 p > 0.80; AB5 - AB1 IBI values, regression: F1,6 = 0.01, R = 0, p > 0.90). In general, then, there appeared to be no consistent increase in IBI values at restored relative to control sites after restoration. It is possible, however, that rainfall amounts in a given wet season affected differences in control vs. restored IBI values during the subsequent spring. The M2 site had IBIs that were larger than or equal to those at the M1 site in all years when both were sampled, including in the two pre-restoration years; however, M2 – M1 IBI differences were lowest (IBIs most similar) in the two driest years (see Figure 14). AB5 values were lower than those at AB1 in the first four years after restoration, but exceeded those at AB1 in the 4th through 6th (2010- 2012) years, before declining in 2013 and 2014 (see Figure 15). These results suggest that restoration effects on IBI scores may be most prominent in wetter years. With the current dataset, however, the M2 – M1 and AB5 – AB1 IBI differences were not significantly related to 2 annual rainfall (linear regression analysis: M2-M1 difference vs. annual rainfall, F1,7 = 2.1, R = 2 0.23, p = 0.19; AB5-AB1 difference vs. annual rainfall, F1,6 = 0.1, R = 0.11, p = 0.70). Although restoration efforts apparently improved habitat quality, they have not yet had a consistent positive effect on BMI communities at M2 and AB5, as measured by IBI score. Over the long-term, we would tend to expect improvements in habitat quality to increase IBI values, because there is a strong relationship between IBI and HA scores across our entire dataset (see

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Figure 9). So, the lack of improvement in IBI scores to date is somewhat puzzling. There do not appear to be issues with water temperature, pH, or dissolved oxygen concentrations at M2 or AB5. Stream flow has been perennial at both sites even in the recent prolonged drought. Despite improvements in many habitat characteristics of M2 and AB5, there are factors that likely limit the improvement of BMI communities at these sites. First, conductivity has been moderately elevated at M2 over the years (1,267 to 1,465 µS), and has been consistently very high at AB5 (3,371 to 4,286 µS), perhaps owing in large part to naturally hard groundwater inputs. Nonetheless, moderate to high conductivity at these sites likely indicates the presence of pollutants from urban runoff that can negatively impact aquatic life, particularly disturbance- sensitive species. On the other hand, three years (2010-2012) of sediment analyses and acute toxicity survivability analyses in old Mission Creek in close proximity to M2 indicated minimal risk to aquatic life. Similar results were obtained at AB estuary just downstream of AB5, as well as in Arroyo Burro Creek at Cliff Dr., which is less than 100 meters from AB5 (City of Santa Barbara, 2014). Another factor that likely has inhibited improvement of the BMI community at M2 and AB5 deals with habitat fragmentation and loss of habitat connectivity. Both restoration sites are small, isolated streams tributary to lower Mission and Arroyo Burro Creeks. Owing to their size and isolation, time will be required for BMIs to colonize either from the mainstem streams, or via aerial colonization from nearby watersheds. It may prove difficult for such colonization to occur, particularly from the mainstems. Lower Mission Creek has a highly impaired BMI community due to intensive habitat degradation including streambed and bank channelization and loss of riparian vegetation, which have caused elevated stream temperatures, increased algal growth, and wide fluctuations in dissolved oxygen concentration including crashes below 2 mg/l in early morning hours (City of Santa Barbara, 2014). Lower Mission Creek is listed as impaired for dissolved oxygen by the Regional Water Quality Control Board, and for toxicity due to Selenastrum (algae) mortality (City of Santa Barbara, 2014). Compared to lower Mission Creek, lower Arroyo Burro has consistently exhibited a more diverse BMI community and higher IBI scores, but it still has consistently scored in the Very Poor to Poor range of the IBI. There has also been significant loss of nearby riparian and upland habitats that are important in the life cycles of many native aquatic invertebrate and vertebrate species, further limiting their ability to colonize and proliferate at the restoration sites. Expectations for restoration of the BMI communities of M2 and AB5 must be realistic. Modest, consistent improvements in IBI scores (e.g., from Very Poor to Poor, or from Poor to Fair) would be considered a success. Channel and riparian restoration at these sites do not address larger scale impairments in hydrology, geomorphology, water quality, habitat continuity and connectivity that have resulted from alteration of their respective watersheds, both of which are more than 70 percent urbanized by land cover. Much of this watershed-scale impairment, and its impact to the stream community, cannot be undone from a practical sense. Whether or not current and future restoration efforts will improve the BMI community and IBI scores at M2 and AB5 can only be evaluated via continued monitoring efforts through time.

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Figure 14: Analyses of Habitat Assessment and IBI Scores for Restoration Site M2 and Control Site

Top: Habitat Assessment Scores (HA, left) and IBI values (right) for the M1 (control) and M2 (restored) sites from 2002 to 2014. Middle: Differences in M2 – M1 HA and IBI values, and annual rainfall (dashed blue line, right graph), for the same time period. Arrows indicate the time of restoration activities. Bottom: M2 – M1 differences in HA values (left) and IBI (right) values versus year and rainfall amounts, respectively. Best fit linear regression lines and associated regression equations, and R2 and p values, are shown.

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Figure 15: Analyses of Habitat Assessment and IBI Scores for Restoration Site AB5 and Control Site

Left: Habitat Assessment Scores (top) and IBI values (bottom) for AB1 (control) and AB5 (restored) sites from 2002 to 2014. Right: Differences in AB5 – AB1 HA (top) and IBI values (bottom), as well as rainfall amounts (bottom right) from 2007 to 2014. The top graph shows the regression line, and associated regression statistics, for the relationship between AB5 – AB1 differences in HA scores and year.

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C. Estuaries Data Analyses 1. Establishing the Sensitivity/Tolerance of Individual BMI taxa and BMI Metrics to Human Disturbance The following presents the results of statistical tests evaluating relationships between BMI parameters and human disturbance using data from study estuaries having salinity of 30 ppt or less. Four estuaries sampled this year had salinities of over 30 ppt. These four sites were excluded from the statistical analyses, as in reviewing the data it was obvious that their BMI community composition did not fit the patterns observed at the remainder of the sites. This is discussed further under “4. Estuaries with Salinities above 30 ppt”. Individual BMI Taxa Results of the ANOVAs of individual BMI taxa by disturbance group are summarized in Table A- 17. Figure 16 illustrates ANOVAs for selected taxa. Based on the results, several taxa were identified as being sensitive to human disturbance within the salinity range of 0-30 ppt, as evidenced by significantly highest mean abundance at REF sites compared to HIGH DIST sites. These taxa are Isopoda (p=0.0045, r2 = 0.34), Amphipoda (p=0.0087, r2 = 0.31), Mystidacea (p=0. 0156, r2 = 0.27), and Acari (p=0.0432, r2 = 0.21). Other taxa having highest mean abundance at REF sites with near significant results (i.e., p>0.05) include Baetidae (p=0.08, r2 = 0.18), Polychaeta (p=0.18, r2 = 0.12), and Aeshnidae (p=0.21, r2 = 0.11). Taxa identified as being tolerant of human disturbance with highest mean at HIGH DIST sites compared to REF sites with significant or near significant results include Ostracoda (p=0.0213, r2 = 0.26), Corixidae (p=0.0463, r2 = 0.21), Oligochaeta (p=0.1943, r2 = 0.12), and Dytisidae (p=0.3159, r2 = 0.09). Cladocera (p=0.6411, r2 = 0.03) had substantially higher mean abundance at HIGH DIST compared to REF sites, but its spotty distribution contributed to relatively low r2 and high p. Chironomidae had significantly highest mean abundance at MOD DIST sites (p=0.0087, r2 = 0.31). Coenagrionidae (p=0.0807, r2 = 0.17) and Libeluliidae (p=0.1079, r2 = 0.16) also had highest mean abundance at MOD DIST sites, although not at a significant level. Gastropoda abundance was highest at REF and HIGH DIST sites and lowest at MOD DIST (p=0.4961, r2 = 0.05), and Copepoda had similar mean abundance for all three disturbance groups. All of these taxa can be considered to have moderate disturbance tolerance at salinities of 0-30 ppt. BMI Metrics Results of the BMI metric ANOVAs by disturbance group are summarized in Table A-18. The seven taxa identified above as being sensitive to human disturbance (Isopoda, Amphipoda, Mystidacea, Acari, Baetidae, Polychaeta, and Aeshnidae) were combined to create the metric % sens BMIs. The five taxa identified above as being tolerant of disturbance (Ostracoda, Corixidae, Oligochaeta, Dytisidae, and Cladocera) were combined to create the metric % tol BMIs. Figure 17 illustrates ANOVAs for % sens BMIs and % tol BMIs.

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Figure 16: ANOVAs of Mean Abundance of Selected BMI Taxa in Estuaries for REF, MOD DIST, and HIGH DIST Groups

Corixidae and Isopoda abundance for each of the three disturbance groups are shown below. Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles. N=29

Corixidae p=0.0463

r2 = 0.21

High Disturbance Tolerance

Isopoda p=0.0045 2 r = 0.34

Low Disturbance

Tolerance

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Figure 17: ANOVAs of Mean Abundance of Selected BMI Metrics in Estuaries for REF, MOD DIST, and HIGH DIST Groups

% sensitive BMIs and % tolerant BMIs for each of the three disturbance groups are shown below. Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles.

P<0.0001 r2 = 0.74 n=29

P<0.0001 r2 = 0.71 n=29

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Metrics with significantly higher mean abundance at REF sites compared to HIGH DIST sites include % sens BMIs (p<0.0001, r2 = 0.74), #sens/#tol taxa (p=0.0026, r2 = 0.37), # sens taxa (p=0.0074, r2 = 0.32), and % cg (p=0.0091, r2 = 0.30). Metrics with significantly higher mean value at HIGH DIST sites compared to REF sites were % tol BMIs (p<0.0001, r2 = 0.71), # tol taxa (p=0.0251, r2 = 0.25) and % pred (p=0.0255, r2 = 0.25). Based on the data collected so far, these seven metrics are sensitive to human disturbance in study area estuaries, and may be suitable for use as core metrics in an IBI that could be developed in the future. % sens BMIs and % tol BMIs thus far have the greatest disturbance sensitivity. BMI density, # overall taxa, % insects, % non-insects, % dominant taxon, and % 2 dominant taxa) do not have significant differences between disturbance groups. These metrics do not trend up or down along a disturbance gradient. Thus far, none of these appear to be candidates as core metrics for a future estuarine IBI.

2. Salinity Effects at REF Sites

The eight REF replicates had a salinity range of 0.8 to 21.7 ppt. Based on the test results, salinity appeared to have little, if any, influence on the potential indicator BMI metrics within this salinity range. % sens BMIs (p=0.8451, r2 = 0.01), % tol BMIs (p=0.7015, r2 = 0.03), # sens taxa/# tol taxa (p=0.7762, r2 = 0.01), and # sens taxa (p=0.9013, r2 = 0.00) had seemingly no correlation with salinity. Figure 18 shows the regression for % sens BMIs vs. salinity. # tol taxa (p=0.5010, r2 = 0.08), % pred (p=0.2346, r2 = 0.23), and % cg (p=0.2875, r2 = 0.18) showed limited correlation with salinity, but not at a significant level. Figure 18: Linear Regression of % Sensitive BMIs vs. Salinity, REF Group (n=8) These test results must be considered preliminary given the low number of replicates, and the fact that they have come from only two distinct estuaries (Jalama and Gaviota). More replication and diversification of REF estuaries having greater physiochemical variability will be needed to gain more confidence in our ability to understand the influences of salinity and other physiochemical parameters on potential indicator BMI metrics. Understanding natural physiochemical influences will be a key step in evaluating the suitability of potential core BMI metrics for inclusion in a future estuarine IBI, as it has been in developing the streams IBI. There are patterns with respect to common, individual BMI taxa and salinity. Gastropoda has been found only in low salinity (5 ppt or less). Baetidae (0.8 to 15 ppt) and Isopoda (0.8 to 21.7 ppt), have been common in low to moderate salinity. Chironimidae, Corixidae, Ostracoda, Oligochaeta, and Amphipoda have been common in all salinities. Polychaeta have been found only in moderate and high salinities (5.5 to 43 ppt).

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3. Year to Year Trends Table A-19 summarizes ANOVA results for % sens BMIs and % tol BMIs by disturbance group for each of the last three years: 2012, 2013, and 2014. Figure 19 illustrates the ANOVAs for % sens BMIs for the three years. There have been wide differences in means in both of these BMI metrics between REF and HIGH DIST sites for all three years. These differences were statistically significant in all cases with the exception of % sens BMIs in 2014 (p=0.1098, r2 = 0.59), where the difference in means for REF sites (40%) and HIGH DIST sites (5%) was considerable. There were only eight replicates for 2014 used in this ANOVA, as four of the 2014 sites had salinity of greater than 30 ppt, and weren’t included. This resulted in a loss of statistical power. % sens BMIs and % tol BMIs have been reliable indicator metrics all three years despite wide physiochemical variability from year to year caused by prolonged drought. Generally, study estuaries have experienced decreasing width, depth, volume, and surface area, and increased salinity over the past three years due to lower freshwater inputs. 4. Estuaries with Salinities above 30 ppt Four of the estuaries surveyed this past year had bottom salinities of greater than 30 ppt. This was the first time that salinities of this level were present in study estuaries. The four high salinity estuaries surveyed include one MOD DIST and three HIGH DIST sites. In reviewing the data from these sites, it was apparent that patterns of BMI composition by disturbance groups observed in lower salinities were not seen in the sites over 30 ppt. For example, Sycamore Creek Estuary (SY) and Goleta Slough (GOL), both HIGH DIST sites, had high % sens BMIs (73 and 70 percent, respectively) and low % tol BMIs (17 and 30 percent, respectively). This is the opposite pattern of what has been consistently observed at HIGH DIST sites in salinities below 30 ppt. High representation from a type of Gammarean Amphipod not previously observed was the primary reason for the high % sens BMIs at SY and GOL. In salinities below 30 ppt, amphipods have been prevalent only at REF sites, and largely absent from MOD DIST and HIGH DIST sites. It is possible that where salinity exceeds 30 ppt, it may become the dominant determining factor of BMI composition. There may be differences in BMI composition attributable to human disturbance in such high salinity conditions as well, but since no high salinity REF sites have been studied, this cannot be determined at this time. More study of high salinity estuaries, and REF sites in particular, will be needed to further explore this.

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Figure 19: ANOVAs of % Sensitive BMIs by Disturbance Group and Year

Top and bottom of diamonds are the 95 percent confidence limits, and the center lines are the means. The lower and upper lines are the 25 percent and 75 percent quantiles.

2012 (p<0.0001, r2 = 0.91, n=12)

2013 (p=0.0083, r2 = 0.80, n=9)

2014 (p=0.1098, r2 = 0.59, n=8)

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V. Closing

Over the past 15 years, the Program has provided a wealth of information regarding the physiochemical habitat conditions and biota (particularly the BMI community) present in local streams. The influences of natural physiochemical and climatic variability and human development on local stream communities have been extensively examined. The following statements can be made based on the research completed thus far: • The updated IBI is highly effective as an indicator of biological integrity, with highly significant relationships with indicies of human disturbance. The IBI has properly differentiated between REF, MOD DIST, and HIGH DIST disturbance groups at a significant level for each year of the Program. • Negative impacts of human land use on local stream communities (particularly BMIs) have been documented with highly significant statistical test results. Degradation of stream communities (e.g., lower IBI scores and loss of sensitive species), as well as physiochemical habitat conditions, has increased linearly with increased watershed development. Urban development has been shown to have greater impacts on stream communities than has agricultural development. • Major episodic disturbances including extreme stream flows, drought conditions, and wildfires have been definitively shown to negatively impact stream communities, as evidenced by lower IBI scores and loss or significant reduction of sensitive BMI and vertebrate taxa following such events. Local stream BMI communities have proven to be resilient, typically showing dramatic recovery from extreme episodic disturbances in a year or two. However, some of the more sensitive species (e.g., rainbow trout) have yet to return to streams impacted by recent wildfires, and may require many years to recover. • Stream habitat restoration sites M2 and AB5 have shown improved habitat conditions, but significant improvements in the BMI community have not occurred thus far at these sites. Channel and riparian restoration at these sites did not address larger scale impairments in hydrology, geomorphology, water quality, habitat continuity and connectivity that have resulted from alteration of their respective watersheds. Much of this watershed-scale impairment cannot be undone from a practical sense. Whether or not current and future restoration efforts will improve the BMI community at M2 and AB5 can only be evaluated via continued monitoring through time. The Program effort to study local estuaries is still relatively new. Based on the limited data set available, the following can be stated thus far: • Seven BMI metrics appear to have promise as indicators of biological integrity for salinities between 0-30 ppt, with significantly different mean abundances between REF and HIGH DIST groups. Some or all of these BMI metrics may be suitable for use as core metrics in an estuarine IBI that could be developed in the future. % sens BMIs and % tol BMIs thus far have the greatest potential, both of which have been significantly different between REF and HIGH DIST groups in each of the three years of study despite wide physiochemical variability from year to year caused by prolonged drought.

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• While salinity certainly has major influences on the composition of the BMI community in local estuaries (i.e., the specific taxa present), thus far it has had no significant effects on any of the potential core BMI metrics within the range of 0-30 ppt. More replication and diversification of REF estuaries having greater physiochemical variability will be needed to gain more confidence in our ability to understand the influences of salinity and other physiochemical parameters on potential indicator BMI metrics. Understanding natural physiochemical influences will be a key step in evaluating the suitability of potential core BMI metrics for inclusion in a future estuarine IBI. • Four of the estuaries surveyed this past year had bottom salinities of greater than 30 ppt. This was the first time that salinities of this level were present in study estuaries. The four high salinity estuaries surveyed include one MOD DIST and three HIGH DIST sites. The four estuaries having salinity of greater than 30 ppt had different BMI composition by disturbance group compared to all the other estuaries. Salinity may become the dominant determining factor of BMI composition where it exceeds 30 ppt. More study of high salinity estuaries, and REF sites in particular, will be needed to further explore this. • Developing a reliable IBI for local estuaries is a major goal of this Program. Accomplishing this will require a greater understanding of relationships between potential core BMI metrics, human disturbance, and the effects of natural physiochemical variables. Based on the progress made thus far, it is hoped this goal will be attained through another two or three years of study.

VI. Acknowledgements

Special thanks to the City of Santa Barbara and County of Santa Barbara for their funding and support of this Program over the last 15 years. George Johnson and Jill Murray of the City, Creeks Division have made substantial contributions in helping determine the scope of work each year and reviewing Program annual reports, as has Cathleen Garnand of the County, Project Clean Water. George Johnson and Willie Brummett (County Project Clean Water) have assisted with field surveys over the years, as has Tommy Liddell (formerly of County Project Clean Water).

Special thanks also to Scott Cooper, Research Professor of Aquatic Ecology at the University of California, Santa Barbara, and Sheila Wiseman, also of UCSB, who completed the analyses of fire impacts on local streams and stream responses to restoration activities, which are presented in this report. Scott also has provided invaluable contributions as a reviewer of analyses, plans, and reports throughout the 15 years of the Program.

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VII. References

Barbour, M.T., J. Gerritsen, B.D. Snyder, and J.B. Stribling. 1999. Rapid Bioassessment Protocols for Use in Creeks and Wadeable Rivers: Periphyton, Benthic Macroinvertebrates and Fish, Second Edition, EPA 841-B-99-002. U.S. Environmental Protection Agency, Office of Water. Washington, D.C. Bowman, M.L., J. Gerritsen, G.R. Gibson, and B.D. Snyder. 2000. Estuarine and Coastal Waters: Bioassessment and Biocriteria Technical Guidance. U.S. Environmental Protection Agency, Office of Water. Washington, D.C. Burt, W.H., and R.P. Grossenheider. 1976. A Field Guide to the Mammals, North America North of Mexico. Third Edition. Houghton Mifflin Company. Boston, New York. California Department of Fish and Game, Aquatic Bioassessment Laboratory. 2002. List of Californian Macroinvertebrate Taxa and Standard Taxonomic Effort. Revised April 30, 2002. City of Santa Barbara. 2014. Fiscal Year 2013 Water Quality Report.

Coombs J.S. and J. M. Melack. 2013. The initial impacts of a wildfire on hydrology and suspended sediment and nutrient export in California chaparral watersheds. Hydrological Processes, 27, 3842–3851.

Cooper, S.D., Dudley T.L., and N. Hemphill. 1986. The Biology of Chaparral Streams in Southern California. Proceedings of the Chaparral Ecosystems Research Conference, May 16-17, 1985, Santa Barbara, California. California Water Resources Center, University of California Santa Barbara. Report No. 62. June, 1986. Cooper, S.D., P. Sam Lake, P.S., Sabater, S., Melack, J.M., and J.L. Sabo. 2013. The effects of land use changes on streams and rivers in Mediterranean climates. Hydrobiologia 719: 383- 425. County of Santa Barbara, Project Clean Water. 2002. Santa Barbara County Coastal Creeks Bioassessment Program, Annual Report, Year 2001. County of Santa Barbara. 2008. Gap Fire Emergency Watershed Response Plan. County of Santa Barbara. 2009. Tea Fire Perimeter Map. County of Santa Barbara. 2009. Jesusita Fire Perimeter Map. Dale, N. 1986. Flowering Plants, the Santa Monica Mountains, Coastal and Chaparral Regions of Southern California. Published by Capra Press in cooperation with the California Native Plant Society. Ecology Consultants, Inc. 2010. Southern Coastal Santa Barbara County Creeks Bioassessment Program, 2009 Report and Updated Index of Biological Integrity. Hickman, J.C. 1993. The Jepson Manual, Higher Plants of California. University of California Press. Berkeley, CA.

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McAuley, M. 1996. Wildflowers of the Santa Monica Mountains. Second Edition. Canyon Publishing Company. Canoga Park, California. Merritt, R.W. and K.W. Cummins. 1996. An Introduction to the Aquatic Insects of North America, Third Edition. Kendall/Hunt Publishing Company. Moyle, P.B. 2002. Inland Fishes of California. University of California Press. Pennak, Robert W. 1953. Freshwater Invertebrates of the United States. The Ronald Press Company. Peterson, R.T. 1990. A Field Guide to Western Birds. Third Edition. Houghton Mifflin Company. Boston, New York. Ranasinghe, J.A., A.M. Barnett, K. Schiff, D.E. Montagne, C. Brantley, C. Beegan, D.B. Cadien, C. Cash, G.B. Deets, D.R. Diener, T.K. Mikel, R.W. Smith, R.G. Velarde, S.D. Watts, and S.B. Weisberg. 2007. Southern California Bight 2003 Regional Monitoring Program: III. Benthic Macrofauna. Southern California Coastal Water Research Project. Costa Mesa, CA.

Smith, Ralph I. and James T. Carlton. 1975. Light’s Manual: Intertidal Invertebrates of the Central California Coast. Third Edition. University of California Press. Stebbins, R.C. 1985. A Field Guide to Western Reptiles and Amphibians. Second Edition. Houghton Mifflin Company. Boston, New York. Stewart, B.P. and C.R. Nelson. 1994. Nymphs of North American Stonefly Genera (Plecoptera). University of North Texas Press. Denton, Texas.

Thompson, B, Weisberg S, Melwani A, Lowe S, Ranasinghe JA, Cadien DB, Dauer DM, Diaz RJ, Fields W, Kellogg M et al.. 2011. Low levels of agreement among experts using best professional judgment to assess benthic condition in the San Francisco Estuary and Delta. Ecological Indicators. 12(1):167-173.

United States Geological Survey. Various dates. 7.5 minute quadrangle topographic maps.

Verkaik, I., M. Rieradevall, S. D. Cooper, J. M. Melack, T. L. Dudley and N. Prat. 2013. Fire as a disturbance in Mediterranean climate streams. Hydrobiologia 719: 353-382.

Weisberg, SB, Thompson B, Ranasinghe JA, Lowe S, Melwani A. 2012. Benthic macrofaunal assemblages of the San Francisco Estuary and Delta, USA. Environmental Monitoring Assessment.

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APPENDIX A:

DATA TABLES

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program Page 67 2014 Report and Updated Index of Biological Integrity

Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Value 5 2 1 0 2 2 0 0 0 2 3 3 1 5 5 S(0-3), M(4-6), T(7-10) M S S S S S S S S S S S S M M Primary FFG cg cg cg cg cg cg p sh p p NA sc sc cf ph Study Reaches Year Disturbance Group Order (ft.) Elevation Gradient watershed area % wilderness % urban % agriculture % herbaceous % undisturbed (ft) width Wet Habitat Score Stream temp. (c) pH Dissolved oxygen (mg/l) Conductivity (microS) Specific cond. (microS @ 25 c) % riparian canopy cover Updated IBI Score Class. of Integrity Core Metrics # EPT families % sens BMIs Tolerance Value Avg. # insect families % sh+pred % PT BMIs tol % Other BMI Metrics %EPT - Baetidae BMI density (#/sq. m) % EPT % Coleoptera % chironomidae % diptera % non-insects % non-insects diptera + % non-insects+chironimidae % cg %sc %sh % cf % pred %sc+sh %sc+sh+pred %cg+sc+sh %cg+cf %cg+pred Individual BMI Taxa Baetidae Caenidae Emphemerellidae Heptagenidae Leptohyphidae Leptophlebiidae Chloroperlidae Nemouridae Perlidae Perlodidae Brachycentridae Glossostomatidae Helicopsychidae Hydropsychidae Hydroptilidae AB2 2000 HIGH DIST 3 75 0.01 4789 60 30 9 1 61 9 83 22.4 8.0 11.8 1580 1663 19 Poor 3 3 6.27 15 8 1 49 2 1320 28 1 30 32 32 64 62 45 14 0 0 8 14 22 58 45 53 80 3 0 0 0 0 0 0 0 0 0 0 0 0 2 AB3 2000 MOD DIST 2 300 0.03 2356 90 3 6 0 90 12 163 17.5 8.0 9.2 1026 1198 53 Good 15 38 4.65 28 15 15 24 35 3591 58 3 18 23 12 35 30 50 7 7 6 8 14 23 65 56 59 69 41 0 2 3 12 0 0 1 0 5 0 0 13 1 AH1 2000 REF 2 150 0.04 2583 100 0 0 0 100 14 168 16.0 7.5 9.8 887 1071 67 Excellent 14 65 3.05 27 32 38 18 53 3670 62 5 16 23 2 26 18 32 10 23 3 9 33 42 64 35 41 25 0 0 18 10 18 6 26 5 0 14 10 3 4 0 AH2 2000 REF 2 240 0.16 2324 100 0 0 0 100 19 182 16.4 7.7 9.2 833 997 55 Good 13 42 4.04 25 11 18 29 32 2672 52 11 11 32 1 33 12 47 3 7 21 5 10 15 57 68 52 62 0 0 8 12 22 2 12 2 0 15 0 2 9 0 C1 2000 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 12 100 18.5 7.6 11.8 1240 1416 13 Poor 3 1 7.27 14 11 0 84 1 322 2 2 53 74 18 92 71 18 2 0 12 11 2 13 20 30 29 4 1 0 0 0 2 0 0 0 0 0 0 0 0 0 C2 2000 MOD DIST 4 50 0.01 9336 83 2 15 0 83 18 120 20.3 6.6 11.9 1083 1190 36 Fair 5 20 5.03 15 16 0 26 19 449 56 13 5 25 3 28 8 58 1 0 17 16 1 17 59 75 74 111 21 2 0 25 9 0 0 0 0 0 0 0 0 0 C3 2000 REF 3 420 0.03 4517 100 0 0 0 100 21 173 16.0 8.6 7.9 539 651 59 Excellent 12 83 2.22 22 18 7 4 45 359 46 31 2 20 0 20 2 77 2 2 0 16 4 20 81 77 93 3 18 40 2 50 4 1 1 0 0 0 0 5 1 0 DP1 2000 MOD DIST 4 40 0.01 4574 88 0 11 1 89 16 120 21.8 7.5 9.2 1340 1427 47 Good 9 49 4.41 19 1 25 30 52 1994 68 1 9 12 18 30 27 62 1 0 5 1 1 2 63 67 63 48 20 0 0 60 0 0 0 0 0 58 0 2 7 4 F1 2000 HIGH DIST 3 10 0.01 5905 57 15 29 0 57 8 26 22.8 8.0 9.7 1204 1257 2 Very Poor 1 0 7.48 6 0 0 99 0 270 0 0 46 47 51 98 97 53 0 0 0 0 0 0 53 53 53 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M1 2000 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 14 80 26.9 8.0 14.9 1220 1177 9 Poor 4 2 6.82 9 1 1 83 1 2640 2 0 18 19 78 97 96 66 14 0 0 1 14 14 80 66 67 4 1 0 0 1 0 0 0 0 0 0 0 0 0 1 M3 2000 MOD DIST 3 400 0.07 4142 79 18 2 0 79 13 157 19.2 8.0 9.1 820 922 63 Excellent 15 45 4.57 29 22 25 33 41 3233 53 6 21 32 3 35 24 34 5 14 11 8 18 27 53 45 43 36 20 0 8 3 17 0 2 0 0 5 7 0 11 0 M4 2000 REF 2 1000 0.08 1376 98 2 0 0 98 14 178 21.2 8.0 8.8 810 873 65 Excellent 14 66 3.04 28 16 14 15 43 5468 52 11 12 19 5 24 17 58 8 4 1 12 12 24 70 58 69 26 40 0 10 5 32 2 0 0 0 14 1 0 2 0 MY1 2000 HIGH DIST 3 130 0.02 3779 81 6 10 4 83 11 110 25.1 8.0 8.9 1260 1258 41 Fair 5 22 4.87 21 7 6 18 20 3000 66 3 10 15 10 25 20 68 6 0 8 7 6 12 73 76 74 137 14 0 0 29 0 0 0 0 0 1 0 0 17 0 MY2 2000 REF 3 290 0.03 2213 96 0 4 0 96 12 168 22.4 7.8 7.4 645 679 61 Excellent 10 44 3.90 26 21 17 13 17 589 40 25 7 25 2 27 9 56 0 6 12 16 6 22 62 68 72 69 0 0 1 0 1 0 2 0 0 1 0 0 21 7 MY3 2000 REF 3 1200 0.13 1316 100 0 0 0 100 14 172 15.4 7.2 9.3 493 604 60 Excellent 15 36 4.66 32 23 15 34 30 2140 42 7 32 35 2 36 33 30 7 6 4 18 13 31 43 33 48 34 4 0 4 6 32 1 5 0 0 2 0 1 10 1 R1 2000 MOD DIST 3 180 0.02 3391 80 8 8 4 81 11 120 21.4 7.8 8.3 1122 1205 50 Good 13 25 5.15 24 6 23 29 41 1976 60 1 24 27 7 34 31 44 4 1 17 5 4 9 48 61 49 57 26 0 2 17 9 0 0 0 0 3 1 0 49 8 R2 2000 REF 3 360 0.04 2840 95 2 3 0 95 13 152 20.2 8.0 9.3 785 864 68 Excellent 18 55 3.25 36 20 22 14 45 5633 49 6 9 21 3 24 13 43 17 9 6 11 27 37 70 49 54 12 26 0 14 14 15 1 6 1 0 5 0 4 15 1 SA1 2000 MOD DIST 3 260 0.03 2867 88 3 3 6 91 15 143 18.6 8.0 9.4 992 1130 47 Good 11 37 4.89 27 9 6 33 29 3000 45 6 15 25 16 41 31 61 5 0 2 10 5 15 66 63 72 49 30 0 0 37 2 0 0 0 0 7 0 0 1 4 SA2 2000 MOD DIST 3 500 0.05 2556 94 0 2 4 96 15 137 20.2 8.0 8.7 1190 1310 63 Excellent 12 63 3.38 31 15 17 12 32 5270 40 17 6 28 6 34 11 63 5 3 6 12 7 20 70 69 75 24 30 0 0 11 5 0 3 0 0 12 0 0 14 0 SJ1 2000 HIGH DIST 4 30 0.01 5169 64 14 20 1 65 27 110 18.4 8.0 8.8 1283 1468 13 Poor 3 4 6.96 12 5 2 72 4 1682 22 2 44 60 10 70 54 29 1 0 17 5 1 6 30 46 34 52 0 0 0 7 0 0 0 0 0 0 0 0 6 0 SJ2 2000 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 12 104 20.5 8.0 10.0 1395 1526 43 Fair 8 32 4.65 18 4 10 26 27 6018 58 10 20 26 3 29 23 61 0 0 12 4 0 4 61 73 65 95 19 0 0 28 3 0 0 0 0 5 0 0 21 0 SJ3 2000 REF 2 1000 0.11 3245 95 1 4 1 95 19 182 16.2 8.0 8.8 735 883 62 Excellent 14 43 4.63 35 27 20 35 27 1908 39 12 29 37 2 39 31 29 1 13 7 14 14 28 43 36 44 36 0 0 5 4 14 1 5 0 0 11 1 0 5 0 SM1 2000 HIGH DIST 2 10 0.01 5945 56 15 28 0 56 8 26 23.2 8.2 8.5 578 599 1 Very Poor 0 0 7.90 6 1 0 97 0 248 0 0 95 97 2 98 97 0 2 0 0 1 2 3 2 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SO1 2000 REF 2 20 0.03 1316 96 0 0 4 98 12 161 17.4 7.8 7.6 839 981 56 Good 9 43 3.76 24 16 10 15 40 977 74 2 7 15 0 15 7 67 2 2 6 14 4 18 71 73 81 101 3 0 17 0 72 20 2 0 0 0 0 0 3 0 SO2 2000 REF 2 500 0.13 1025 96 0 0 4 98 17 189 17.6 7.7 7.3 730 850 55 Good 10 38 3.72 25 14 12 9 26 1328 69 2 6 15 0 15 6 61 5 1 3 13 7 19 68 64 74 131 8 0 8 0 26 20 3 0 0 0 0 0 6 0 T1 2000 HIGH DIST 3 30 0.01 3616 75 4 19 2 76 16 80 18.3 7.5 9.7 1705 1955 41 Fair 7 53 4.14 19 6 2 34 52 5238 61 3 5 7 27 34 32 86 0 1 2 5 1 6 87 88 91 26 58 0 0 90 2 0 0 0 0 0 0 0 2 0 T2 2000 MOD DIST 3 110 0.02 3221 81 0 18 1 82 8 120 25.2 8.0 9.8 1673 1667 52 Good 8 52 3.92 21 11 11 12 46 4048 69 2 8 22 4 25 11 72 1 4 7 7 5 12 77 79 79 69 30 0 0 74 0 0 0 0 0 0 0 0 16 2 AB2 2001 HIGH DIST 3 75 0.01 4789 60 30 9 1 61 15 70 18.0 8.4 838 967 8 Very Poor 2 1 7.55 11 6 0 87 0 603 7 5 61 76 9 84 70 15 1 0 14 6 1 6 16 29 21 19 0 0 0 0 1 0 0 0 0 0 0 0 0 0 AB3 2001 MOD DIST 2 300 0.03 2356 90 3 6 0 90 13 171 16.3 7.8 828 993 51 Good 11 20 5.42 31 27 7 35 17 819 38 10 28 41 2 43 30 35 0 2 6 25 3 27 38 41 60 63 18 3 2 0 6 0 1 0 5 0 0 0 6 0 AH1 2001 REF 2 150 0.04 2583 100 0 0 0 100 12 170 18.4 7.8 638 730 47 Good 11 27 5.36 23 19 10 51 15 782 28 5 47 61 3 64 49 24 2 3 4 16 4 20 28 28 40 39 0 0 4 3 7 11 5 8 0 0 0 0 2 0 AT1 2001 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 31 60 18.3 8.0 1692 1940 4 Very Poor 1 1 7.88 9 4 0 94 0 1528 1 1 76 81 12 93 89 13 0 0 3 5 0 5 13 16 18 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2001 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 21 92 19.3 8.4 1413 1586 15 Poor 2 4 7.01 11 7 4 70 4 303 11 2 59 78 8 86 67 22 1 0 5 7 1 8 23 27 29 20 0 0 0 0 0 0 0 0 0 0 0 0 0 12 C1 2001 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 20 111 18.0 8.4 1102 1272 4 Very Poor 2 1 7.69 10 3 0 94 0 841 1 2 81 90 7 97 88 8 1 0 7 3 1 4 9 14 10 2 1 0 0 0 0 0 0 0 0 0 0 0 0 0 C2 2001 MOD DIST 4 50 0.01 9336 83 2 15 0 83 20 122 16.1 7.5 667 804 11 Poor 3 2 7.30 11 6 0 85 2 770 8 4 64 80 6 86 70 14 0 0 15 6 0 6 15 29 20 20 0 3 0 0 2 0 0 0 0 0 0 0 0 0 C3 2001 REF 3 420 0.03 4517 100 0 0 0 100 18 175 15.1 7.8 345 425 57 Good 18 41 4.41 34 14 9 32 25 1594 44 11 27 40 1 41 28 50 2 1 6 13 3 16 52 55 63 57 2 12 16 11 6 1 1 4 1 1 1 4 3 0 SJ1 2001 HIGH DIST 4 30 0.01 5169 64 14 20 1 65 16 109 17.6 7.8 1055 1229 20 Poor 4 14 6.70 18 7 2 75 10 578 15 5 59 76 2 78 61 15 1 0 14 7 1 8 16 30 22 14 0 0 0 25 0 0 0 0 0 0 1 0 4 0 SJ2 2001 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 11 97 16.7 8.4 992 1179 23 Poor 9 5 6.84 23 5 2 77 4 1320 17 3 47 78 0 78 47 16 0 0 30 5 1 5 17 46 21 38 1 0 3 1 1 0 0 0 0 0 0 0 3 0 SJ3 2001 REF 2 1000 0.11 3245 95 1 4 1 95 19 179 15.3 7.8 656 805 64 Excellent 15 34 4.42 32 29 20 27 26 1327 52 8 24 30 3 33 26 38 3 16 3 13 19 32 57 41 51 78 2 0 2 1 13 2 41 0 1 3 0 0 2 0 SO2 2001 REF 2 500 0.13 1025 96 0 0 4 98 18 188 15.7 8.1 567 689 59 Excellent 12 32 4.05 26 18 18 20 22 917 60 2 12 28 1 29 13 46 8 4 8 14 13 27 59 54 60 115 1 0 2 0 9 26 6 0 0 0 1 0 4 1 AB1 2002 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 15 71 16.6 7.9 6.9 1350 1608 12 Poor 3 0 7.13 13 8 1 71 1 3438 15 5 35 35 36 72 71 45 5 0 0 11 5 16 51 46 56 44 0 0 0 0 0 0 0 0 0 0 0 0 1 1 AB2 2002 HIGH DIST 3 75 0.01 4789 60 30 9 1 61 17 101 13.6 8.0 8.1 976 1248 11 Poor 2 3 7.45 13 7 0 84 0 1054 2 2 28 46 48 95 76 49 2 0 10 7 2 9 52 59 56 5 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB3 2002 MOD DIST 2 300 0.03 2356 90 3 6 0 90 11 168 13.4 8.2 8.5 1097 1409 60 Excellent 15 41 4.71 31 22 16 37 36 1579 42 3 17 29 20 49 37 51 3 9 4 13 12 25 63 55 64 18 37 3 1 3 15 2 0 0 3 2 0 0 9 0 AH1 2002 REF 2 150 0.04 2583 100 0 0 0 100 12 169 11.6 8.4 9.6 773 1039 69 Excellent 15 58 3.55 29 25 22 25 48 1579 56 2 25 38 0 38 25 38 4 10 0 14 14 28 52 38 53 22 13 1 24 16 26 23 2 3 0 1 0 2 0 0 AT1 2002 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 19 75 14.1 7.7 3.9 2023 2559 1 Very Poor 0 1 8.55 4 0 0 99 0 6875 0 0 33 34 66 99 99 65 0 0 0 0 0 0 65 65 65 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2002 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 7 74 16.9 7.9 7.7 1840 2178 3 Very Poor 1 1 7.79 8 4 0 95 0 1908 1 0 88 89 7 96 95 8 0 1 0 3 1 4 9 8 11 4 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C1 2002 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 15 102 13.8 7.8 6.7 1206 1521 5 Very Poor 1 3 7.55 12 4 0 84 0 909 1 2 32 44 52 96 84 48 7 0 6 4 7 11 55 55 52 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2002 REF 3 420 0.03 4517 100 0 0 0 100 20 170 12.7 8.5 10.3 529 693 69 Excellent 18 66 3.04 28 18 34 14 59 2895 72 8 11 15 2 17 12 49 7 6 5 12 13 25 62 54 61 38 27 0 33 11 4 1 2 12 0 28 2 17 11 0 EC1 2002 MOD DIST 3 10 0.02 3915 93 2 0 5 96 12 134 13.7 7.8 7.0 938 1198 43 Fair 10 28 5.31 26 15 6 46 25 522 39 5 15 18 32 49 47 59 7 0 1 15 8 22 67 60 74 42 16 0 5 26 11 0 0 0 0 0 2 4 2 0 GAV1 2002 MOD DIST 3 25 0.01 12791 59 0 0 41 79 13 140 19.1 8.2 11.7 1434 1617 53 Good 8 33 4.76 22 17 15 24 40 1988 52 2 15 23 6 29 21 43 5 1 9 16 6 22 49 52 59 37 1 0 0 75 0 0 0 0 0 0 0 0 23 2 GAV2 2002 MOD DIST 3 260 0.02 10828 54 0 0 46 77 13 126 24.8 8.2 9.6 1542 1548 49 Good 9 39 4.92 22 11 16 35 45 831 52 0 29 36 3 39 32 43 2 1 12 10 3 12 45 55 52 20 18 0 0 71 0 0 0 0 0 0 0 0 34 5 M1 2002 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 18 81 22.6 8.0 15.9 1252 1313 3 Very Poor 1 0 8.08 6 5 0 99 0 1886 1 0 73 73 20 93 93 19 0 0 1 5 0 6 19 20 24 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2002 HIGH DIST 1 50 0.02 643 24 76 0 0 24 8 64 17.5 7.7 4.1 1172 1367 8 Very Poor 2 0 7.62 6 2 5 85 5 1429 12 0 77 79 8 87 85 11 0 0 1 2 0 3 11 11 13 21 0 0 0 0 0 0 0 0 0 0 0 0 0 15 M3 2002 MOD DIST 3 400 0.07 4142 79 18 2 0 79 13 157 15.9 8.0 8.1 895 1083 61 Excellent 11 48 3.73 29 25 11 22 39 2200 40 4 12 21 9 30 21 43 18 8 0 17 25 42 68 43 60 6 48 0 8 17 10 0 0 0 0 2 2 0 0 0 RIN1 2002 MOD DIST 3 220 0.02 8131 83 0 16 1 84 14 128 14.9 7.7 8.6 894 1108 57 Good 14 49 4.22 29 14 9 33 43 1579 53 3 7 14 27 40 33 71 4 4 2 9 8 17 79 73 81 28 61 0 1 37 5 0 0 1 1 0 0 0 2 1 SJ1 2002 HIGH DIST 4 30 0.01 5169 64 14 20 1 65 8 72 11.0 8.0 7.5 1069 1459 16 Poor 2 8 7.07 16 13 0 79 1 791 2 3 63 76 11 88 74 15 1 0 4 13 1 15 16 19 28 3 0 0 0 4 0 0 0 0 0 0 0 0 0 0 SJ2 2002 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 11 107 17.4 7.9 10.0 1387 1623 41 Fair 9 28 5.54 23 11 8 51 22 1404 33 4 33 43 19 62 52 47 3 1 3 10 4 14 51 49 56 31 12 0 0 30 0 0 0 0 0 9 0 3 5 0 SJ3 2002 REF 2 1000 0.11 3245 95 1 4 1 95 22 177 12.0 8.4 9.8 724 965 67 Excellent 17 59 3.64 31 20 20 22 52 873 59 8 19 21 7 28 26 48 8 9 2 10 17 27 65 50 58 21 73 1 16 3 2 0 0 0 0 7 0 3 5 1 SO2 2002 REF 2 500 0.13 1025 96 0 0 4 98 8 179 13.8 8.2 9.3 793 1008 68 Excellent 15 54 3.56 29 27 24 23 46 3438 54 1 21 28 1 30 23 34 12 14 0 13 26 39 60 35 48 22 19 0 21 0 28 7 1 0 1 5 4 0 1 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-1 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Value 5 2 1 0 2 2 0 0 0 2 3 3 1 5 5 S(0-3), M(4-6), T(7-10) M S S S S S S S S S S S S M M Primary FFG cg cg cg cg cg cg p sh p p NA sc sc cf ph Study Reaches Year Disturbance Group Order (ft.) Elevation Gradient watershed area % wilderness % urban % agriculture % herbaceous % undisturbed (ft) width Wet Habitat Score Stream temp. (c) pH Dissolved oxygen (mg/l) Conductivity (microS) Specific cond. (microS @ 25 c) % riparian canopy cover Updated IBI Score Class. of Integrity Core Metrics # EPT families % sens BMIs Tolerance Value Avg. # insect families % sh+pred % PT BMIs tol % Other BMI Metrics %EPT - Baetidae BMI density (#/sq. m) % EPT % Coleoptera % chironomidae % diptera % non-insects % non-insects diptera + % non-insects+chironimidae % cg %sc %sh % cf % pred %sc+sh %sc+sh+pred %cg+sc+sh %cg+cf %cg+pred Individual BMI Taxa Baetidae Caenidae Emphemerellidae Heptagenidae Leptohyphidae Leptophlebiidae Chloroperlidae Nemouridae Perlidae Perlodidae Brachycentridae Glossostomatidae Helicopsychidae Hydropsychidae Hydroptilidae SY1 2002 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 9 84 15.1 8.4 8.9 2545 3140 23 Poor 4 6 6.55 18 10 5 71 5 1170 6 2 25 30 59 89 83 47 14 4 1 7 18 26 65 48 54 3 0 0 0 0 0 0 0 0 0 0 0 0 1 0 AB1 2003 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 14 104 17.4 8.6 10.6 1696 1985 40 12 Poor 1 2 6.34 8 5 0 55 0 1535 37 3 10 23 36 59 46 70 1 0 12 5 1 7 71 82 75 112 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB2 2003 HIGH DIST 3 75 0.01 4789 60 30 9 1 61 15 84 16.0 8.4 6.8 1356 1637 87 11 Poor 2 2 6.86 12 3 0 64 0 2158 31 1 43 48 16 64 59 47 0 0 4 4 0 4 47 51 51 93 0 0 0 0 1 0 0 0 0 0 0 0 0 0 AB3 2003 MOD DIST 2 300 0.03 2356 90 3 6 0 90 9 158 15.7 8.7 9.7 789 960 92 32 Fair 7 11 5.80 22 10 2 44 7 1339 41 4 20 42 10 51 29 47 3 1 19 9 4 13 51 66 56 103 0 0 1 0 14 0 0 0 0 1 0 0 1 0 AH1 2003 REF 2 150 0.04 2583 100 0 0 0 100 14 174 15.5 8.8 9.2 710 868 100 69 Excellent 14 62 3.20 28 31 28 16 51 553 68 4 12 19 1 21 13 47 4 20 4 11 23 34 70 51 58 52 1 0 24 5 40 6 6 5 0 0 0 1 1 0 AT1 2003 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 18 83 20.7 8.4 9.4 2516 2744 18 0 Very Poor 0 0 8.69 1 0 0 96 0 2444 0 0 10 10 90 100 100 86 4 0 0 0 4 4 90 86 86 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2003 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 11 58 21.4 8.5 11.6 1917 2060 37 6 Very Poor 1 0 6.89 6 2 0 62 0 1587 36 0 13 31 32 63 45 66 1 0 18 2 1 3 67 84 68 108 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C1 2003 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 21 113 14.7 8.2 9.7 662 824 66 7 Very Poor 3 4 7.74 13 1 0 93 2 1092 2 0 77 82 13 95 90 18 0 0 1 1 0 1 18 18 19 1 3 0 0 0 3 0 0 0 0 0 0 0 0 0 C3 2003 REF 3 420 0.03 4517 100 0 0 0 100 23 174 14.3 8.5 9.3 497 624 81 63 Excellent 16 44 3.79 28 15 14 15 37 1902 72 5 11 19 3 22 14 65 1 6 2 8 8 16 72 67 73 103 19 1 30 5 16 0 5 3 1 0 0 2 0 2 GAV1 2003 MOD DIST 3 25 0.01 12791 59 0 0 41 79 13 157 18.5 8.6 9.7 1397 1593 15 41 Fair 8 20 5.38 20 11 10 36 24 791 51 2 22 34 5 39 27 46 1 1 17 10 2 13 49 63 57 81 3 0 0 40 0 0 0 0 0 0 0 0 20 3 M1 2003 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 13 88 19.3 8.2 12.3 1210 1358 27 0 Very Poor 1 0 7.68 3 0 0 90 0 952 5 0 59 68 27 95 86 26 5 0 10 0 5 5 31 35 26 14 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2003 HIGH DIST 1 50 0.02 643 24 76 0 0 24 9 79 21.8 8.4 8.1 1280 1364 68 4 Very Poor 2 0 7.61 6 4 1 91 1 1249 6 0 76 88 4 92 80 7 0 0 12 4 0 4 7 19 11 13 0 0 0 0 0 0 0 0 0 0 0 0 0 4 M3 2003 MOD DIST 3 400 0.07 4142 79 18 2 0 79 15 157 15.7 8.9 9.5 802 975 93 46 Good 13 19 5.50 21 14 12 40 16 1058 51 3 24 38 6 43 29 44 3 9 14 5 12 17 56 58 49 105 2 0 5 1 5 0 0 0 0 1 3 0 1 1 MONT1 2003 MOD DIST 3 350 0.05 3465 82 17 1 0 82 10 133 18.4 7.9 8.4 845 968 93 62 Excellent 17 38 4.36 28 22 30 23 35 1980 46 6 10 17 26 43 36 37 18 11 7 11 29 40 66 44 48 31 3 0 5 4 4 0 1 1 0 5 11 0 4 10 SA2 2003 MOD DIST 3 500 0.05 2556 94 0 2 4 96 7 152 18.8 8.9 8.9 898 1019 68 54 Good 12 26 4.68 27 17 11 16 23 511 66 10 12 16 5 21 17 61 1 2 2 15 3 18 65 63 76 129 4 0 5 2 24 0 0 0 5 10 0 0 6 5 SJ1 2003 HIGH DIST 4 30 0.01 5169 64 14 20 1 65 14 90 12.6 8.3 10.5 724 948 39 14 Poor 3 2 6.88 14 5 0 64 1 1191 30 1 54 60 7 68 61 36 1 0 4 5 1 5 37 40 41 87 0 0 0 2 0 0 0 0 0 0 0 0 1 0 SJ2 2003 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 13 106 15.6 8.1 10.2 634 772 70 31 Fair 10 9 6.04 22 7 3 47 8 709 45 2 39 49 1 51 41 44 1 1 8 5 2 7 46 51 49 112 3 0 2 7 1 0 1 0 0 3 0 0 3 0 SJ3 2003 REF 2 1000 0.11 3245 95 1 4 1 95 20 178 14.8 8.9 9.2 696 864 86 51 Good 10 32 4.86 26 19 10 39 21 572 42 10 21 41 4 45 24 40 2 5 17 14 7 21 46 57 54 64 8 0 3 1 21 0 5 0 0 0 0 0 0 0 SO2 2003 REF 2 500 0.13 1025 96 0 0 4 98 12 181 15.6 9.0 9.2 819 1000 93 65 Excellent 12 56 3.22 30 31 27 20 46 1325 63 3 10 25 0 25 11 42 5 18 10 13 23 36 65 51 55 49 11 0 18 0 30 14 34 0 0 0 1 0 2 0 SY1 2003 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 14 95 16.0 8.5 11.6 1786 2158 80 27 Poor 5 4 6.26 15 7 5 49 5 1323 45 4 36 48 2 50 38 43 0 2 13 5 2 7 45 56 48 120 1 0 0 0 0 0 0 0 0 0 0 0 0 0 SY2 2003 HIGH DIST 3 200 0.03 1956 52 46 2 0 52 15 109 14.3 8.3 9.7 1291 1624 72 27 Poor 8 5 5.94 18 6 2 40 3 1476 53 2 24 41 3 44 27 54 1 1 14 5 2 7 56 68 59 150 1 0 0 0 1 0 0 0 0 1 0 0 1 0 AB1 2005 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 13 99 16.9 7.8 8.9 1797 2125 70 20 Poor 4 1 5.75 11 3 1 35 2 165 63 1 6 33 1 34 7 63 0 0 28 3 0 3 63 91 65 182 0 0 0 0 1 0 0 0 0 0 0 0 3 0 AB2 2005 HIGH DIST 3 75 0.01 4789 60 30 9 1 61 15 107 16.9 7.8 8.5 1344 1592 90 13 Poor 3 0 6.05 9 1 1 45 1 198 53 0 12 43 1 44 13 54 0 0 32 1 0 1 54 85 55 156 0 0 1 0 0 0 0 0 0 0 0 0 0 0 AB3 2005 MOD DIST 2 300 0.03 2356 90 3 6 0 90 15 174 17.1 8.2 9.6 928 1094 93 30 Poor 7 6 5.67 13 5 9 37 10 330 61 1 15 38 0 38 15 52 0 3 27 2 3 5 55 80 55 153 0 0 0 0 3 1 6 0 0 0 0 0 15 0 AH1 2005 REF 2 150 0.04 2583 100 0 0 0 100 15 170 14.6 8.5 9.4 603 751 96 37 Fair 6 8 5.13 17 7 5 16 5 679 79 1 14 18 0 18 14 76 0 2 2 6 2 8 78 78 82 222 0 0 1 0 0 7 5 0 1 0 0 0 0 0 AT1 2005 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 28 76 17.0 8.5 12.0 905 1073 33 10 Very Poor 1 2 6.64 6 1 0 48 0 297 50 1 13 18 31 49 44 81 0 0 4 1 0 1 81 85 82 149 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2005 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 17 66 16.9 7.9 6.0 1703 2014 23 8 Very Poor 2 0 6.68 9 2 0 50 0 372 47 1 20 23 28 51 48 75 0 0 2 2 1 2 75 77 76 141 0 0 0 0 0 0 0 0 0 0 0 0 0 1 C1 2005 MOD DIST 4 15 0.01 9598 80 3 17 0 80 22 125 17.2 8.7 9.6 606 712 78 12 Very Poor 2 1 6.27 8 1 1 44 1 238 54 1 42 45 0 45 42 54 0 1 2 1 1 1 54 56 54 160 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2005 REF 3 420 0.03 4517 100 0 0 0 100 22 163 10.6 8.7 10.7 466 645 92 26 Poor 8 4 5.82 15 3 2 33 3 743 64 2 33 34 0 34 33 64 0 1 0 2 1 3 64 64 66 181 0 0 1 1 2 1 2 0 0 1 0 0 0 0 GAV1 2005 HIGH DIST 3 25 0.01 12791 59 0 0 41 79 16 115 15.2 8.5 9.3 1006 1240 0 12 Poor 1 1 6.15 7 1 0 39 0 495 58 0 37 41 0 41 37 58 0 0 2 1 0 1 58 60 59 174 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M1 2005 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 19 85 23.0 8.0 13.8 1183 1229 43 3 Very Poor 1 0 7.03 5 1 0 70 0 110 29 0 62 69 1 70 63 30 0 0 7 1 0 1 30 37 30 88 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2005 HIGH DIST 1 50 0.02 643 24 76 0 0 24 9 110 22.4 7.7 10.5 1350 1423 18 12 Poor 2 0 5.97 6 0 1 43 1 248 57 0 11 41 1 43 12 58 0 0 30 0 0 0 58 88 58 169 0 0 0 0 0 0 0 0 0 0 0 0 0 2 M3 2005 MOD DIST 3 400 0.07 4142 79 18 2 0 79 16 165 15.7 8.2 9.5 796 969 88 36 Fair 9 13 5.53 17 8 4 36 15 141 58 2 19 36 0 36 19 54 0 2 19 6 2 8 56 73 60 129 2 1 0 0 28 0 0 0 0 0 0 0 5 0 MONT1 2005 MOD DIST 3 350 0.05 3465 82 17 1 0 82 16 139 13.3 8.7 10.0 456 588 94 23 Poor 6 5 5.74 15 2 0 31 4 610 67 1 30 32 0 32 30 67 0 0 0 2 0 2 67 67 69 189 1 1 1 0 7 0 0 0 0 0 0 0 0 0 SA2 2005 MOD DIST 3 500 0.05 2556 94 0 2 4 96 14 163 13.2 8.8 10.3 669 867 88 34 Fair 7 7 5.41 18 7 3 23 5 595 71 4 22 24 0 24 22 68 1 2 1 5 3 8 71 69 73 195 0 0 0 0 6 0 6 0 1 0 0 0 0 1 SJ1 2005 HIGH DIST 4 30 0.01 5169 64 14 20 1 65 14 92 12.6 8.3 9.8 1139 1492 49 15 Poor 4 2 6.45 12 2 1 51 2 175 46 1 39 47 5 52 44 51 0 0 7 2 0 2 51 58 53 133 0 0 0 0 4 0 0 0 0 0 0 0 1 0 SJ2 2005 MOD DIST 3 120 0.01 3836 81 1 16 1 82 14 125 14.4 8.3 10.2 1032 1291 97 32 Fair 4 7 4.99 15 9 1 13 2 53 72 8 8 11 4 15 12 77 2 1 1 8 3 11 80 78 85 104 1 0 0 0 0 0 1 0 0 0 0 0 0 0 SJ3 2005 REF 2 1000 0.11 3245 95 1 4 1 95 15 186 14.1 8.5 10.0 565 716 96 47 Good 8 19 4.99 15 18 16 28 19 229 68 2 23 27 2 29 25 54 0 14 4 4 14 18 69 58 58 149 0 0 1 0 8 0 37 0 0 0 0 0 0 0 SY1 2005 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 14 110 17.5 8.4 11.7 2388 2791 97 23 Poor 3 3 5.88 13 5 2 36 2 198 56 5 25 36 1 37 26 55 1 0 11 5 1 6 56 67 61 161 0 0 0 0 0 0 0 0 0 1 0 0 5 0 SY2 2005 HIGH DIST 3 200 0.03 1956 52 46 2 0 52 15 116 17.9 8.3 9.4 1594 1846 87 16 Poor 1 1 5.67 6 3 0 28 0 270 68 2 8 26 2 28 10 69 0 0 18 3 0 3 69 88 72 205 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB1 2006 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 14 104 17.4 7.9 11.1 1596 1869 70 18 Poor 3 1 6.00 13 2 1 36 1 819 59 0 23 33 7 39 29 64 1 0 9 2 1 3 65 73 66 174 0 0 0 0 0 0 0 0 0 0 0 0 2 0 AB3 2006 MOD DIST 2 300 0.03 2356 90 3 6 0 90 13 168 15.4 8.3 10.9 859 1054 96 42 Fair 6 26 4.92 16 12 7 21 22 330 71 1 17 19 4 23 21 67 2 7 0 6 8 14 76 68 73 144 22 1 0 0 24 0 0 0 0 0 0 0 0 0 AB4 2006 HIGH DIST 2 190 0.01 2631 82 13 5 0 82 13 95 17.1 8.3 12.6 984 1161 98 13 Poor 2 2 6.60 10 6 0 55 1 580 37 2 47 51 8 59 55 41 2 0 1 6 2 8 43 43 47 106 4 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2006 REF 2 150 0.04 2583 100 0 0 0 100 23 188 18.1 NM 10.1 699 807 99 68 Excellent 14 60 3.47 26 31 32 15 51 360 74 1 13 22 1 23 14 44 1 21 0 10 22 33 66 44 54 68 3 0 11 0 44 18 1 1 0 0 1 2 0 4 AT1 2006 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 24 88 17.6 8.7 10.5 897 1035 41 6 Very Poor 2 2 7.20 10 1 0 75 0 485 21 1 69 72 4 77 73 27 0 0 1 1 0 1 27 28 28 62 0 0 1 0 0 0 0 0 0 0 0 0 0 0 AT2 2006 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 17 59 18.3 8.3 7.7 1402 1609 37 13 Poor 2 1 6.40 12 3 1 55 1 1684 41 0 25 50 7 57 32 45 1 1 23 2 2 4 47 68 47 119 0 0 0 0 0 0 0 0 0 0 0 0 0 3 C1 2006 MOD DIST 4 15 0.01 9598 80 3 17 0 80 19 125 17.7 8.4 12.5 689 803 74 19 Poor 6 4 6.52 14 5 1 57 5 833 38 4 45 53 4 57 49 41 0 0 6 5 0 5 41 47 46 99 4 0 4 2 1 0 0 0 0 0 0 0 0 3 C3 2006 REF 3 420 0.03 4517 100 0 0 0 100 22 166 16.0 8.5 10.7 565 682 93 62 Excellent 14 47 3.46 22 17 16 7 42 457 80 5 6 14 1 15 8 69 1 9 4 8 9 18 78 72 77 111 6 9 32 2 29 0 14 0 0 0 0 1 2 3 M1 2006 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 19 85 23.0 8.0 13.8 1183 1229 43 6 Very Poor 3 1 7.49 6 1 0 83 1 580 15 0 75 77 7 84 82 22 0 0 2 1 0 1 22 24 22 44 0 0 0 0 1 0 0 0 0 0 0 0 0 0 M2 2006 HIGH DIST 1 50 0.02 643 24 76 0 0 24 9 110 22.4 7.7 10.5 1350 1423 18 9 Very Poor 2 0 6.65 6 1 1 54 1 848 46 0 49 50 4 54 53 49 0 0 1 1 0 1 49 50 50 135 0 0 0 0 0 0 0 0 0 0 0 0 2 0 M3 2006 MOD DIST 3 400 0.07 4142 79 18 2 0 79 16 165 15.7 8.2 9.5 796 969 88 53 Good 14 31 4.37 22 9 11 14 29 742 82 2 12 13 2 15 14 74 3 5 0 4 8 13 83 75 79 159 7 2 5 0 40 0 6 0 1 0 4 0 0 1 M7 2006 HIGH DIST 1 45 0.02 645 24 76 0 0 24 11 92 16.9 7.7 7.9 1226 1449 83 6 Very Poor 1 1 6.80 5 1 0 59 0 189 40 0 49 50 10 60 59 49 0 0 0 1 0 1 50 50 50 108 0 0 0 0 0 0 0 0 0 0 0 0 0 0 MONT2 2006 MOD DIST 3 160 0.03 4040 74 25 1 0 74 18 132 17.2 8.5 10.9 717 844 79 33 Fair 10 12 6.29 21 11 4 54 10 699 35 5 48 52 6 58 54 39 1 2 0 10 3 13 42 39 48 75 3 0 2 0 11 0 0 0 3 0 1 0 0 0 RIN1 2006 MOD DIST 3 220 0.02 8131 83 0 16 1 84 14 137 15.8 8.2 10.1 674 817 100 52 Good 14 22 4.73 22 14 9 20 21 516 69 7 5 23 0 23 5 63 0 4 17 9 4 14 67 80 72 145 8 1 2 2 22 1 7 1 0 0 0 0 1 3 SA2 2006 MOD DIST 3 500 0.05 2556 94 0 2 4 96 12 157 16.7 10.7 756 899 94 49 Good 11 46 4.08 17 8 6 16 45 330 80 1 12 15 3 18 15 79 0 4 1 3 4 8 84 80 83 104 38 0 1 2 76 0 10 0 1 0 0 0 0 0 SJ1 2006 HIGH DIST 4 30 0.01 5169 64 14 20 1 65 13 115 16.7 8.1 11.3 1440 1714 60 23 Poor 7 10 6.73 17 10 1 66 5 424 22 4 57 61 11 72 68 30 0 0 2 10 0 11 30 31 40 50 1 0 3 5 4 0 0 0 0 1 0 0 2 0 SJ2 2006 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 13 114 16.7 7.9 11.0 1336 1590 90 41 Fair 11 23 5.39 25 9 4 42 18 1191 45 6 33 42 4 45 36 47 1 1 7 8 2 10 49 55 55 83 10 0 7 4 20 0 2 0 0 1 0 0 2 2 SJ3 2006 REF 2 1000 0.11 3245 95 1 4 1 95 25 182 13.6 NM 11.0 562 719 93 56 Good 13 33 4.38 26 14 11 21 22 321 62 7 18 25 1 26 19 60 2 5 3 9 7 16 67 63 69 120 4 1 5 0 24 0 10 0 0 5 0 0 1 2

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-2 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Value 5 2 1 0 2 2 0 0 0 2 3 3 1 5 5 S(0-3), M(4-6), T(7-10) M S S S S S S S S S S S S M M Primary FFG cg cg cg cg cg cg p sh p p NA sc sc cf ph Study Reaches Year Disturbance Group Order (ft.) Elevation Gradient watershed area % wilderness % urban % agriculture % herbaceous % undisturbed (ft) width Wet Habitat Score Stream temp. (c) pH Dissolved oxygen (mg/l) Conductivity (microS) Specific cond. (microS @ 25 c) % riparian canopy cover Updated IBI Score Class. of Integrity Core Metrics # EPT families % sens BMIs Tolerance Value Avg. # insect families % sh+pred % PT BMIs tol % Other BMI Metrics %EPT - Baetidae BMI density (#/sq. m) % EPT % Coleoptera % chironomidae % diptera % non-insects % non-insects diptera + % non-insects+chironimidae % cg %sc %sh % cf % pred %sc+sh %sc+sh+pred %cg+sc+sh %cg+cf %cg+pred Individual BMI Taxa Baetidae Caenidae Emphemerellidae Heptagenidae Leptohyphidae Leptophlebiidae Chloroperlidae Nemouridae Perlidae Perlodidae Brachycentridae Glossostomatidae Helicopsychidae Hydropsychidae Hydroptilidae SY1 2006 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 14 110 17.5 8.4 11.7 2388 2791 97 31 Fair 5 3 5.41 15 7 3 18 3 129 75 3 12 18 4 21 16 75 1 1 4 5 3 8 78 79 80 164 1 0 0 0 0 0 0 0 0 0 0 0 1 0 SY2 2006 MOD DIST 3 170 0.03 1956 52 46 2 0 52 15 120 17.9 8.3 9.4 1594 1846 87 29 Fair 5 2 5.59 13 4 5 24 7 827 70 3 16 25 2 26 18 66 1 0 12 4 1 5 66 78 70 191 1 0 0 0 3 0 0 0 0 0 0 0 1 0 T2 2006 MOD DIST 3 110 0.02 3221 81 0 18 1 82 16 131 21.0 8.4 12.1 1043 1131 73 40 Fair 8 9 5.77 19 22 6 35 11 352 43 17 21 28 6 34 27 41 0 0 12 22 0 22 41 53 63 96 2 0 1 3 10 0 0 0 0 0 0 0 8 4 AB1 2007 MOD DIST 3 25 0.01 5646 51 38 7 4 53 12 122 17.4 7.7 7.5 1656 1936 55 15 Poor 2 3 6.26 12 4 1 53 1 679 41 1 16 36 20 56 36 60 0 0 18 4 0 4 61 78 64 121 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB3 2007 MOD DIST 2 300 0.03 2356 90 3 6 0 90 8 155 13.7 7.7 6.5 1618 2063 94 24 Poor 6 5 6.70 18 12 4 77 4 1486 5 3 24 31 54 85 78 50 6 1 6 12 7 19 57 56 62 3 0 0 0 0 1 0 0 0 0 0 0 0 0 0 AB4 2007 HIGH DIST 2 190 0.01 2631 82 13 5 0 82 10 106 17.6 7.5 3.8 1431 1666 93 3 Very Poor 1 3 7.91 9 2 0 93 0 617 0 0 20 22 73 95 93 70 3 0 0 2 3 5 73 70 72 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB5 2007 HIGH DIST 1 10 0.02 275 30 70 0 0 30 7 67 18.6 7.6 9.6 3610 4270 7 9 Very Poor 1 1 6.75 11 5 0 66 0 283 22 2 33 38 35 73 68 57 0 0 4 5 0 6 58 61 63 67 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2007 REF 2 150 0.04 2583 100 0 0 0 100 13 173 13.5 8.4 7.1 741 948 91 60 Excellent 14 49 4.29 24 25 13 34 33 3667 41 2 32 37 14 51 46 31 8 4 0 21 12 33 43 31 51 24 16 0 19 7 18 4 0 5 0 0 1 10 0 4 AT1 2007 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 33 84 17.4 8.3 1.9 1045 1217 28 2 Very Poor 0 1 7.74 8 2 0 95 0 3300 0 0 24 24 72 96 95 69 2 0 0 2 2 4 71 69 71 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2007 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 16 78 16.3 8.2 6.5 1330 1600 60 15 Poor 3 4 6.77 16 5 2 70 2 4714 17 1 29 39 42 81 71 49 5 0 7 5 5 10 55 56 54 44 0 0 0 0 0 0 0 0 0 0 0 0 1 5 C1 2007 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 16 88 18.8 8.2 5.0 1000 1200 50 6 Very Poor 2 2 7.53 10 3 0 91 0 2870 1 1 11 14 80 94 91 76 3 0 0 3 3 6 79 77 80 2 0 0 0 1 0 0 0 0 0 0 0 0 0 0 C3 2007 REF 3 420 0.03 4517 100 0 0 0 100 15 151 14.7 8.6 8.0 550 684 88 68 Excellent 18 69 3.15 32 20 19 14 58 2683 61 7 7 13 16 29 23 59 6 7 3 13 13 26 72 62 72 10 39 0 34 18 25 0 1 3 0 2 5 1 6 9 GAV1 2007 MOD DIST 3 25 0.01 12791 59 0 0 41 79 19 162 24.3 8.1 13.2 1903 1930 7 51 Good 9 39 4.31 19 8 15 18 50 1886 69 3 13 14 5 19 18 62 3 0 11 8 3 11 65 73 70 59 67 0 0 38 0 0 0 0 1 0 0 0 25 6 GAV1 2007 MOD DIST 3 25 0.01 12791 59 0 0 41 79 9 131 18.5 8.1 6.7 1345 1540 42 46 Good 9 40 4.86 20 11 11 35 45 3667 50 0 22 24 20 44 42 55 4 3 4 8 7 15 62 59 63 14 57 0 0 45 0 0 0 0 0 0 0 0 5 9 M1 2007 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 19 98 23.0 7.8 9.6 1183 1228 71 7 Very Poor 2 3 7.21 6 1 1 77 1 721 18 0 58 68 14 82 72 30 1 0 7 1 2 3 32 37 31 52 0 0 0 0 0 0 0 0 0 0 0 0 0 3 M2 2007 HIGH DIST 1 50 0.02 643 24 76 0 0 24 10 110 17.4 7.5 6.2 1119 1308 36 8 Poor 2 1 7.26 8 2 3 79 3 793 19 0 55 68 13 81 68 28 0 1 12 1 1 2 29 40 29 48 0 0 0 0 0 0 0 0 0 0 0 0 0 8 M3 2007 MOD DIST 3 400 0.07 4142 79 18 2 0 79 15 156 16.3 7.7 8.5 984 1183 89 49 Good 11 37 4.92 24 12 14 46 29 480 36 6 22 26 24 51 47 53 11 5 1 7 15 22 69 54 60 21 23 0 2 0 21 0 0 0 0 0 15 0 1 1 M4 2007 REF 2 1000 0.08 1376 98 2 0 0 98 13 176 15.7 8.1 9.3 749 908 99 64 Excellent 14 56 3.86 26 30 31 29 42 1158 50 9 27 32 3 35 30 31 10 21 1 9 31 40 61 32 40 22 1 7 15 1 9 1 6 0 0 0 20 0 0 0 M7 2007 HIGH DIST 1 45 0.02 645 24 76 0 0 24 9 106 17.7 7.7 6.8 1135 1319 84 8 Very Poor 2 1 7.06 6 1 3 76 3 233 22 0 44 69 8 77 52 26 0 0 25 0 1 1 27 52 27 43 0 0 0 0 0 0 0 0 0 0 0 0 0 7 MONT2 2007 HIGH DIST 3 160 0.03 4040 74 25 1 0 74 11 114 16.8 8.5 6.3 952 1129 81 23 Poor 5 14 5.95 16 13 1 55 2 3667 3 4 6 10 81 91 87 54 26 0 0 13 26 39 80 54 66 3 0 0 2 0 1 0 0 0 0 0 0 0 0 0 RIN1 2007 MOD DIST 3 220 0.02 8131 83 0 16 1 84 10 139 14.5 8.2 6.6 800 1010 90 57 Good 17 51 4.13 26 17 7 30 40 4583 43 2 7 12 40 52 47 62 12 2 2 15 14 28 75 63 76 9 30 1 4 50 14 0 2 3 0 0 1 0 1 1 SA2 2007 MOD DIST 3 500 0.05 2556 94 0 2 4 96 8 125 14.9 8.3 6.3 800 983 80 49 Good 13 27 5.51 32 23 16 53 20 7333 21 2 6 10 59 69 65 53 13 12 0 11 25 36 78 53 64 1 2 1 1 0 10 0 1 0 0 3 0 0 0 4 SJ2 2007 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 10 88 15.8 8.3 2.8 795 1085 66 24 Poor 8 11 6.96 24 8 2 72 8 2538 10 1 18 23 61 84 79 60 8 0 1 8 9 16 68 61 67 7 11 0 0 7 0 0 0 0 0 1 0 1 1 0 SJ3 2007 REF 2 1000 0.11 3245 95 1 4 1 95 11 168 13.0 8.6 8.0 698 906 87 56 Good 14 42 4.35 32 24 12 33 19 1737 22 11 25 29 26 55 51 31 14 3 2 21 17 38 48 33 52 9 8 0 9 2 4 0 0 0 0 2 0 1 6 3 SY1 2007 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 9 102 14.8 8.1 8.3 2092 2594 93 22 Poor 4 6 6.14 15 12 2 56 2 333 14 2 14 25 57 82 72 52 16 0 6 11 16 28 68 58 63 36 0 0 0 0 0 0 0 0 0 0 0 0 3 0 SY2 2007 MOD DIST 3 170 0.03 1956 52 46 2 0 52 10 128 16.3 7.8 8.7 1755 2105 95 23 Poor 4 4 6.28 19 10 2 54 2 1054 22 3 15 22 47 70 62 53 14 0 6 9 14 23 67 59 63 59 0 0 0 0 0 0 0 0 0 0 0 0 0 0 T3 2007 HIGH DIST 3 90 0.01 3300 79 1 19 1 80 13 81 18.4 8.5 8.7 1175 1346 83 26 Poor 8 12 6.37 18 9 4 68 12 4125 14 3 17 19 61 80 78 57 9 1 3 8 10 17 67 60 65 5 5 0 0 14 4 0 0 0 0 0 0 0 5 2 AB1 2008 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 17 118 17.2 7.7 11.0 1871 2198 78 18 Poor 4 3 7.18 13 6 4 66 4 595 28 2 27 31 36 67 63 57 1 0 6 6 1 7 58 63 64 70 0 0 0 0 0 0 0 0 0 0 0 0 6 0 AB3 2008 MOD DIST 2 300 0.03 2356 90 3 6 0 90 13 159 11.9 8.1 9.5 999 1335 93 22 Poor 7 5 6.13 15 4 1 48 5 1000 48 2 28 47 1 48 29 48 0 0 18 4 0 4 48 66 52 129 1 0 0 0 10 0 0 0 1 0 0 0 1 1 AB4 2008 HIGH DIST 2 190 0.01 2631 82 13 5 0 82 7 103 18.6 7.2 6.1 1257 1425 98 1 Very Poor 1 0 7.67 6 2 0 87 0 398 1 0 46 47 49 96 95 40 10 0 0 2 10 13 50 40 42 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB5 2008 HIGH DIST 1 10 0.02 275 30 70 0 0 30 6 82 19.1 7.2 10.5 3803 4286 19 4 Very Poor 1 3 7.45 9 2 0 89 0 1031 4 1 69 75 18 93 87 21 2 0 4 2 2 4 23 25 23 12 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2008 REF 2 150 0.04 2583 100 0 0 0 100 11 164 14.8 8.6 9.3 745 931 93 59 Excellent 14 46 3.95 26 16 9 20 38 943 64 3 18 25 3 28 21 58 5 3 2 13 8 21 66 59 71 81 16 0 13 18 36 11 3 1 0 0 4 2 0 0 AT1 2008 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 30 70 24.6 8.6 17.0 2004 2043 12 2 Very Poor 2 1 8.08 4 0 0 98 0 468 1 0 64 64 35 99 99 33 1 0 0 0 1 1 34 33 34 1 0 0 0 0 1 0 0 0 0 0 0 0 0 0 AT2 2008 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 12 78 18.9 8.2 8.1 1233 1394 23 26 Poor 3 3 6.73 14 20 5 61 5 478 13 1 45 71 11 82 56 17 4 0 7 20 4 24 20 24 37 24 0 0 0 0 0 0 0 0 0 0 0 0 1 15 C1 2008 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 15 103 20.3 8.2 11.9 1356 1491 55 9 Very Poor 3 2 7.52 12 4 0 87 1 943 5 3 81 85 6 91 87 10 2 0 1 4 2 7 12 11 14 14 1 0 0 1 0 0 0 0 0 0 0 0 0 0 C3 2008 REF 3 420 0.03 4517 100 0 0 0 100 12 152 16.1 8.6 8.3 552 665 76 56 Good 15 41 4.55 28 13 8 32 37 1100 57 5 26 34 1 35 27 53 1 4 6 9 5 14 58 59 62 65 9 6 10 28 28 0 6 2 0 0 2 0 3 0 GAV1 2008 MOD DIST 3 25 0.01 12791 59 0 0 41 79 16 161 16.0 8.0 9.7 1499 1813 33 33 Fair 6 16 5.86 17 10 6 47 14 251 40 2 37 50 1 51 38 36 0 0 15 10 0 10 36 51 46 80 5 0 0 17 2 0 0 0 0 0 0 0 18 0 GAV1 2008 MOD DIST 3 25 0.01 12791 59 0 0 41 79 13 129 20.6 8.2 9.6 1482 1619 60 38 Fair 9 25 5.60 22 11 4 47 23 165 39 6 39 46 3 49 42 40 0 0 5 11 0 12 40 45 51 50 11 0 5 26 13 1 0 0 0 0 0 0 10 1 M1 2008 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 20 94 23.8 8.0 10.4 1227 1257 65 0 Very Poor 1 0 7.96 5 0 0 97 0 429 2 0 91 91 6 97 97 6 1 0 0 0 1 1 7 6 6 6 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2008 HIGH DIST 1 50 0.02 643 24 76 0 0 24 10 107 18.5 7.7 7.3 1176 1346 27 12 Poor 2 1 7.10 6 3 8 73 8 1100 23 0 63 72 3 75 67 16 1 0 8 2 1 4 17 24 18 43 0 0 0 0 0 0 0 0 0 0 0 0 0 25 M3 2008 MOD DIST 3 400 0.07 4142 79 18 2 0 79 13 170 17.3 8.1 6.8 964 1130 99 56 Good 13 27 4.84 28 20 14 29 26 1941 54 6 24 30 0 30 24 42 6 6 5 14 12 26 54 47 56 86 4 0 11 1 17 0 3 0 0 0 5 0 4 2 M4 2008 REF 2 1000 0.08 1376 98 2 0 0 98 17 183 14.2 8.1 8.7 626 791 98 51 Good 12 43 4.74 18 21 17 44 34 363 46 6 43 44 1 45 44 35 0 14 1 6 14 21 50 36 42 35 1 6 4 0 40 2 3 0 0 0 0 0 1 0 M7 2008 HIGH DIST 1 45 0.02 645 24 76 0 0 24 7 99 19.1 7.8 7.5 1199 1351 94 7 Very Poor 2 2 7.43 8 4 0 86 0 379 8 0 71 84 4 88 75 10 1 0 12 4 1 5 12 22 15 23 0 0 0 0 0 0 0 0 0 0 0 0 0 1 MONT2 2008 MOD DIST 3 160 0.03 4040 74 25 1 0 74 12 121 15.2 8.4 8.7 754 930 75 29 Fair 5 7 6.04 13 20 1 45 2 402 30 16 27 41 11 52 38 37 3 0 12 20 3 23 40 49 57 79 0 0 1 0 4 0 0 0 0 0 0 0 0 0 RIN1 2008 MOD DIST 3 220 0.02 8131 83 0 16 1 84 13 124 12.8 8.3 9.1 690 900 98 38 Fair 9 16 5.88 24 17 3 53 11 1100 28 11 37 56 1 57 38 28 2 2 15 15 4 19 32 43 43 50 15 0 2 3 4 0 5 1 0 0 2 0 0 0 SA2 2008 MOD DIST 3 500 0.05 2556 94 0 2 4 96 25 141 15.3 8.3 9.2 879 1078 73 51 Good 8 48 4.16 22 23 3 23 42 413 54 15 21 24 1 25 22 54 0 1 0 23 1 24 55 54 77 33 6 0 9 0 101 0 0 0 6 0 0 0 1 0 SJ2 2008 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 12 96 16.8 8.3 8.9 1322 1569 99 33 Fair 10 15 5.84 23 7 2 46 11 1100 44 4 33 41 7 47 40 51 1 1 7 6 1 7 53 58 57 98 8 0 3 2 14 0 0 1 0 0 1 0 3 0 SY1 2008 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 12 96 21.0 8.3 5.6 2890 3121 94 13 Poor 2 3 6.73 12 6 1 60 1 1467 27 4 46 47 14 61 59 36 6 1 0 6 7 13 42 36 42 53 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SY2 2008 MOD DIST 3 170 0.03 1956 52 46 2 0 52 10 129 18.3 7.8 5.3 1834 2101 100 16 Poor 2 2 7.06 15 12 0 68 0 569 14 7 52 54 9 62 60 18 5 0 0 12 5 17 23 18 30 42 0 0 0 0 0 0 0 0 0 0 0 0 0 0 T3 2008 HIGH DIST 3 90 0.01 3300 79 1 19 1 80 10 94 18.1 8.3 10.8 994 1145 62 43 Fair 12 10 5.11 24 10 3 13 9 868 20 6 8 11 60 72 68 75 2 1 3 9 2 12 77 78 84 31 1 0 1 5 13 0 0 0 0 2 0 0 1 1 AB1 2009 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 17 116 14.6 7.7 6.5 1599 1997 85 16 Poor 2 3 6.35 10 7 2 57 2 410 35 1 23 41 22 63 45 53 1 0 16 7 1 7 54 69 60 100 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB3 2009 MOD DIST 2 300 0.03 2356 90 3 6 0 90 15 153 15.7 8.0 10.1 1326 1613 93 12 Poor 2 3 6.75 9 10 0 71 0 682 13 8 39 72 7 79 46 16 4 0 29 10 4 14 20 45 26 38 0 0 0 0 1 0 0 0 0 0 0 0 0 0 AB5 2009 HIGH DIST 1 10 0.02 275 30 70 0 0 30 7 103 15.3 7.2 7.6 3260 4002 45 13 Poor 1 3 6.85 12 12 0 64 0 165 13 5 45 55 20 76 65 31 3 0 2 12 3 15 34 33 43 39 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB6 2009 HIGH DIST 3 155 0.02 4390 64 25 10 1 65 11 104 18.5 9.0 8.6 1003 1145 92 10 Very Poor 1 4 7.19 12 8 0 71 0 126 1 0 30 38 47 86 78 31 18 0 4 9 18 27 50 35 40 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2009 REF 2 150 0.04 2583 100 0 0 0 100 8 165 16.5 8.4 9.0 895 1071 97 63 Excellent 11 63 3.17 28 20 14 18 54 156 63 2 16 22 0 22 17 52 8 8 0 11 16 27 68 52 63 23 38 0 19 30 41 14 3 2 0 0 0 0 0 0 AT1 2009 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 25 85 18.9 8.5 2.8 1533 1735 37 0 Very Poor 0 0 7.92 4 0 0 97 0 107 0 0 89 90 10 100 99 8 2 0 0 0 2 2 10 8 9 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2009 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 6 85 16.4 8.4 7.6 1154 1385 78 5 Very Poor 1 2 7.00 9 3 0 90 0 76 5 0 19 44 49 93 68 55 1 0 20 4 1 5 56 75 58 11 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C1 2009 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 20 93 21.5 8.0 5.2 1396 1496 71 0 Very Poor 0 0 7.68 2 0 0 100 0 270 0 0 0 24 76 100 76 64 0 0 24 0 0 0 64 88 64 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-3 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Value 5 2 1 0 2 2 0 0 0 2 3 3 1 5 5 S(0-3), M(4-6), T(7-10) M S S S S S S S S S S S S M M Primary FFG cg cg cg cg cg cg p sh p p NA sc sc cf ph Study Reaches Year Disturbance Group Order (ft.) Elevation Gradient watershed area % wilderness % urban % agriculture % herbaceous % undisturbed (ft) width Wet Habitat Score Stream temp. (c) pH Dissolved oxygen (mg/l) Conductivity (microS) Specific cond. (microS @ 25 c) % riparian canopy cover Updated IBI Score Class. of Integrity Core Metrics # EPT families % sens BMIs Tolerance Value Avg. # insect families % sh+pred % PT BMIs tol % Other BMI Metrics %EPT - Baetidae BMI density (#/sq. m) % EPT % Coleoptera % chironomidae % diptera % non-insects % non-insects diptera + % non-insects+chironimidae % cg %sc %sh % cf % pred %sc+sh %sc+sh+pred %cg+sc+sh %cg+cf %cg+pred Individual BMI Taxa Baetidae Caenidae Emphemerellidae Heptagenidae Leptohyphidae Leptophlebiidae Chloroperlidae Nemouridae Perlidae Perlodidae Brachycentridae Glossostomatidae Helicopsychidae Hydropsychidae Hydroptilidae C3 2009 REF 3 420 0.03 4517 100 0 0 0 100 9 154 18.5 8.4 7.3 631 723 70 65 Excellent 15 69 2.88 26 17 13 5 57 198 75 7 2 7 5 12 7 72 6 9 1 8 15 23 87 73 80 55 51 3 5 40 31 0 0 1 0 0 2 5 1 0 GAV1 2009 MOD DIST 3 25 0.01 12791 59 0 0 41 79 11 124 20.1 8.0 6.3 1623 1793 50 39 Fair 9 26 5.49 21 6 6 43 29 372 45 2 34 37 12 49 46 51 1 0 3 5 2 7 53 54 56 49 21 0 0 41 7 0 0 0 0 0 0 0 9 3 M1 2009 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 17 106 15.8 7.7 10.6 1189 1445 49 4 Very Poor 1 1 7.45 7 1 0 84 0 165 13 0 77 82 4 86 81 16 1 0 3 1 1 1 17 19 17 38 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2009 HIGH DIST 1 50 0.02 643 24 76 0 0 24 10 115 19.4 7.9 9.8 1242 1390 73 13 Poor 2 1 6.59 8 2 6 60 6 821 33 0 41 60 5 65 46 28 4 0 18 2 4 6 32 45 29 81 0 0 0 0 0 0 0 0 0 0 0 0 0 19 M3 2009 MOD DIST 3 400 0.07 4142 79 18 2 0 79 15 160 10.3 8.0 9.1 908 1261 97 48 Good 12 31 5.23 26 12 13 44 27 783 46 2 32 38 9 47 41 43 4 5 7 7 9 16 52 49 50 57 11 0 0 0 31 0 3 0 0 0 6 0 1 2 M4 2009 REF 2 1000 0.08 1376 98 2 0 0 98 19 142 12.2 8.5 9.3 700 926 98 62 Excellent 11 45 4.37 28 28 23 37 36 248 43 7 29 38 4 41 33 31 2 18 6 11 20 31 52 38 42 18 2 6 0 0 31 2 19 0 0 0 1 0 0 0 M7 2009 HIGH DIST 1 45 0.02 645 24 76 0 0 24 13 100 15.7 7.9 8.8 1128 1364 94 4 Very Poor 1 1 7.14 6 0 0 74 0 672 24 0 63 72 4 76 67 27 1 0 8 0 1 1 28 35 27 71 0 0 0 0 0 0 0 0 0 0 0 0 0 0 MONT2 2009 MOD DIST 3 160 0.03 4040 74 25 1 0 74 16 127 15.7 8.4 9.0 992 1204 87 24 Poor 3 7 6.02 17 16 1 45 2 114 9 13 12 16 56 72 69 38 27 1 1 15 28 43 66 39 53 21 0 0 0 0 2 0 0 0 0 0 0 0 0 0 RIN0 2009 MOD DIST 4 50 0.01 11071 75 0 25 0 75 11 148 15.5 7.9 12.0 1712 2092 51 30 Fair 7 27 5.32 13 2 8 48 26 946 42 1 7 17 40 57 48 78 3 1 9 1 3 5 82 88 80 43 32 1 0 29 0 0 0 0 0 0 0 0 22 0 RIN1 2009 MOD DIST 3 220 0.02 8131 83 0 16 1 84 10 120 17.8 8.1 8.0 865 1009 94 29 Fair 6 32 5.49 16 6 2 54 27 248 31 4 36 42 20 62 56 49 6 2 2 4 8 12 57 51 54 14 25 0 0 11 38 0 0 0 0 0 0 0 0 0 SA2 2009 MOD DIST 3 500 0.05 2556 94 0 2 4 96 7 130 13.9 7.8 5.3 1512 1916 62 31 Fair 10 12 6.26 25 11 4 77 6 156 9 1 4 7 73 80 78 77 3 2 2 10 5 15 82 79 87 8 0 0 2 1 2 0 0 0 1 0 0 0 3 0 SJ2 2009 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 7 81 18.1 8.2 7.2 1556 1792 93 25 Poor 4 16 5.95 14 13 1 52 7 59 31 5 39 51 2 52 41 34 2 0 11 13 2 15 37 45 47 31 0 0 0 6 2 0 0 0 0 0 0 0 1 0 SJ3 2009 REF 2 1000 0.11 3245 95 1 4 1 95 16 172 13.7 8.4 7.0 709 905 95 62 Excellent 13 53 3.65 25 33 16 21 38 182 50 4 15 18 9 27 24 44 6 12 1 21 18 39 62 45 64 30 20 5 13 1 14 0 6 0 0 0 0 0 1 0 SY1 2009 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 11 70 18.6 8.4 10.5 2188 2489 98 8 Very Poor 3 0 6.85 10 2 1 67 1 930 29 1 40 64 5 69 46 33 0 0 21 2 0 2 33 54 36 83 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SY2 2009 HIGH DIST 3 170 0.03 1956 52 46 2 0 52 15 106 17.9 8.1 10.3 1901 2206 85 18 Poor 3 3 6.11 12 4 1 42 1 1191 49 1 28 45 2 46 30 51 0 0 13 4 0 4 51 63 55 144 0 0 0 0 0 0 0 0 0 0 0 0 0 0 T3 2009 HIGH DIST 3 90 0.01 3300 79 1 19 1 80 7 84 16.4 8.3 8.5 1194 1433 85 15 Poor 2 2 7.22 8 18 0 75 0 175 6 11 72 75 2 77 75 9 0 0 0 19 0 19 9 9 28 17 1 0 0 0 0 0 0 0 0 0 0 0 0 0 AB1 2010 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 4 108 17.9 8.0 9.3 1428 1654 79 17 Poor 3 1 6.66 12 3 8 64 8 2538 32 0 30 58 6 64 36 29 0 0 35 3 0 3 29 64 32 72 0 0 0 0 0 0 0 0 0 0 0 0 13 0 AB2 2010 HIGH DIST 3 75 0.01 4789 60 30 9 1 61 6 98 21.1 8.0 8.9 1420 1535 85 14 Poor 3 0 6.82 13 4 4 71 4 2538 23 2 38 71 1 72 39 20 0 0 35 4 0 4 20 55 24 57 0 0 0 0 0 0 0 0 0 0 0 0 5 0 AB3 2010 MOD DIST 2 300 0.03 2356 90 3 6 0 90 4 127 19.1 8.5 10.9 956 1079 44 14 Poor 4 2 6.28 10 1 2 60 2 2200 38 0 11 61 0 61 11 37 0 0 50 1 0 1 37 87 38 108 0 0 0 0 0 0 1 0 0 1 0 0 5 0 AB5 2010 HIGH DIST 1 10 0.02 275 30 70 0 0 30 2 117 15.9 7.2 6.8 3008 3598 83 2 Very Poor 1 1 7.62 9 1 0 93 0 1833 4 1 69 81 13 94 82 17 0 0 12 2 0 2 17 29 19 11 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB7 2010 HIGH DIST 1 55 0.01 330 17 43 2 38 36 3 107 16.5 7.9 7.8 1426 1704 100 11 Poor 3 2 7.31 12 4 2 86 2 1650 8 0 59 76 12 88 71 17 2 0 17 4 2 6 19 34 20 18 0 0 0 0 0 0 0 0 0 0 0 0 4 1 AH1 2010 REF 2 150 0.04 2583 100 0 0 0 100 17 160 15.8 8.4 8.7 765 929 96 67 Excellent 14 65 3.59 26 27 24 26 52 680 59 2 25 30 1 31 26 36 7 20 2 7 27 34 64 38 43 20 8 0 20 7 49 6 6 1 0 0 0 1 2 0 AP1 2010 MOD DIST 2 75 0.04 2300 74 1 23 2 75 8 137 15.6 8.3 10.4 1560 1937 48 21 Poor 6 6 6.26 17 8 1 59 5 868 18 5 18 57 15 72 33 20 14 0 37 8 14 22 34 56 27 40 1 0 0 1 11 0 0 0 0 0 0 0 0 0 AT1 2010 HIGH DIST 4 15 0.00 12443 48 39 7 6 51 22 78 21 8.3 11.1 2327 2523 43 0 Very Poor 1 0 8.59 4 1 0 98 0 1833 0 1 26 26 73 99 99 72 1 0 0 1 1 2 73 72 73 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2010 HIGH DIST 3 50 0.01 2393 12 73 7 8 16 8 96 20.7 8.1 8.4 1944 2047 60 6 Very Poor 2 0 6.92 8 1 1 75 1 1031 24 0 26 65 10 75 36 33 0 0 39 1 0 1 34 72 34 70 0 0 0 0 0 0 0 0 0 0 0 0 0 2 C1 2010 HIGH DIST 4 15 0.01 9598 80 3 17 0 80 18 100 19.1 8 14.1 1366 1538 75 1 Very Poor 1 0 6.67 5 2 0 57 0 485 0 0 45 48 52 100 97 11 40 0 2 2 40 42 51 12 12 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2010 REF 3 420 0.03 4517 100 0 0 0 100 18 183 15.7 8.4 7.9 573 694 90 61 Excellent 16 42 4.46 27 16 15 27 39 485 62 6 18 23 5 28 23 52 6 5 6 11 10 21 62 58 63 68 14 3 9 8 38 0 0 0 0 1 9 5 2 3 GAV1 2010 MOD DIST 3 25 0.01 12791 59 0 0 41 79 12 124 18.3 8.2 9.7 1474 1690 65 31 Poor 6 26 5.80 16 14 1 50 18 77 36 1 43 45 6 52 50 41 0 0 1 13 0 14 42 42 54 41 10 0 0 22 5 0 0 0 0 0 0 0 0 1 M1 2010 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 3 69 24.3 8.0 8.9 1329 1349 54 4 Very Poor 1 1 7.30 9 1 0 83 0 3000 14 0 63 83 1 84 64 16 0 0 18 1 0 1 16 34 17 42 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2010 HIGH DIST 1 50 0.02 643 24 76 0 0 24 3 119 20.0 7.9 9.5 1148 1267 72 5 Very Poor 2 0 6.98 7 2 1 76 1 3300 21 0 46 75 3 78 49 21 1 0 28 2 1 3 22 49 23 58 0 0 0 0 0 0 0 0 0 0 0 0 0 4 M3 2010 MOD DIST 3 400 0.07 4142 79 18 2 0 79 6 151 21.6 8.4 8.9 990 1060 89 20 Poor 6 4 6.46 16 3 3 59 3 1833 36 1 43 60 0 60 43 35 1 1 17 2 2 4 36 52 37 99 0 0 0 0 0 0 2 0 0 0 0 0 3 1 M4 2010 REF 2 1000 0.08 1376 98 2 0 0 98 4 158 14.0 8.3 9.7 611 775 100 13 Poor 3 6 6.63 12 4 1 66 3 1031 28 2 55 68 0 69 55 29 1 1 11 3 2 5 31 40 32 76 0 0 0 0 7 0 2 0 0 0 0 0 0 0 MONT2 2010 HIGH DIST 3 160 0.03 4040 74 25 1 0 74 9 85 18.2 8.6 9 889 1021 68 11 Poor 3 5 7.00 14 5 0 75 1 99 18 2 51 71 6 77 57 28 0 0 15 4 0 5 29 43 33 42 0 0 0 0 1 0 0 0 0 0 0 0 1 0 RIN0 2010 MOD DIST 4 50 0.01 11071 75 0 25 0 75 5 136 18.7 8.1 12.9 1396 1588 81 25 Poor 6 1 5.88 12 3 6 37 6 786 60 3 16 36 1 37 17 55 1 0 23 3 1 4 55 78 58 161 0 0 0 1 0 0 0 0 0 1 0 0 12 3 RIN1 2010 MOD DIST 3 220 0.02 8131 83 0 16 1 84 14 128 15.5 8 8.63 749 915 93 49 Good 11 37 4.89 25 13 9 33 36 384 60 2 30 32 3 35 33 52 2 7 0 6 10 16 62 53 58 71 14 1 8 22 35 0 0 0 0 2 0 0 0 0 SA2 2010 MOD DIST 3 500 0.05 2556 94 0 2 4 96 15 138 19.3 8.4 8.3 890 1000 43 28 Poor 6 6 6.36 19 9 5 53 7 77 38 3 44 53 2 55 47 34 0 2 9 7 3 10 37 43 41 68 0 0 0 0 3 0 3 0 0 0 0 0 4 2 SJ2 2010 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 17 83 15.3 8 10.33 1219 1497 87 37 Fair 8 7 6.33 21 30 6 55 8 943 17 2 43 77 2 78 45 13 0 4 10 27 4 31 17 23 40 28 0 0 0 5 1 0 3 0 0 2 0 0 2 2 SJ3 2010 REF 2 1000 0.11 3245 95 1 4 1 95 13 176 12.4 8.5 9.1 667 879 95 56 Good 9 48 4.38 24 27 18 39 33 327 42 6 35 36 7 43 42 33 3 17 0 10 21 31 53 33 43 26 1 0 7 0 38 0 32 0 0 0 0 0 0 0 SY1 2010 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 4 93 18.6 8.2 10.7 1659 2078 88 11 Poor 2 1 6.47 9 1 1 54 1 1571 43 1 37 52 3 55 40 46 0 0 15 1 0 1 46 61 47 125 0 0 0 0 0 0 0 0 0 0 0 0 2 0 SY2 2010 MOD DIST 3 170 0.03 1956 52 46 2 0 52 5 130 14.9 8.1 11.7 1315 1560 78 22 Poor 6 1 6.38 13 3 8 54 8 3667 44 1 32 52 1 53 33 36 0 1 27 3 1 4 37 63 39 107 0 0 0 0 0 0 0 0 0 0 1 0 20 1 T3 2010 HIGH DIST 3 90 0.01 3300 79 1 19 1 80 9 62 20.2 8.4 9 933 1022 94 19 Poor 3 1 5.96 8 3 2 32 2 81 64 2 25 28 6 33 31 67 0 0 4 3 0 3 68 71 70 150 0 0 0 0 0 0 1 0 0 0 0 0 5 0 AB1 2011 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 6 99 18.6 8.1 10.3 1705 1940 97 6 Very Poor 1 1 7.36 10 6 0 78 0 263 17 3 25 26 51 77 76 68 0 0 0 5 0 5 68 68 73 45 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB3 2011 MOD DIST 2 300 0.03 2356 90 3 6 0 90 4 161 16.6 8.5 11.0 938 1116 68 33 Fair 8 4 5.91 15 6 11 37 11 660 59 2 27 37 1 38 28 48 1 2 18 4 2 6 50 66 52 142 0 0 0 0 1 0 2 0 2 1 0 0 18 0 AB5 2011 HIGH DIST 1 10 0.02 275 30 70 0 0 30 1 101 14.5 7.2 6.1 3236 4051 94 11 Poor 1 2 7.35 11 12 0 83 0 375 0 10 57 66 24 89 81 22 2 0 5 12 2 14 24 27 34 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB7 2011 HIGH DIST 1 55 0.01 330 17 43 2 38 36 2 103 23.2 7.9 8.1 1468 1519 100 15 Poor 2 2 6.57 9 8 1 50 1 223 35 0 38 43 16 58 53 41 4 0 3 8 4 12 45 44 49 75 0 0 0 0 0 0 0 0 0 0 0 0 3 0 AH1 2011 REF 2 150 0.04 2583 100 0 0 0 100 3 160 13.3 8.3 6.2 666 858 92 61 Excellent 14 36 4.18 27 18 15 18 31 423 73 1 14 23 0 23 14 59 1 6 5 12 7 19 67 64 71 126 1 0 15 3 30 17 4 5 0 0 1 0 0 1 C1 2011 MOD DIST 4 15 0.01 9598 80 3 17 0 80 6 142 14.2 7.7 7.4 1382 1743 77 11 Poor 5 10 6.91 10 1 0 76 9 600 22 0 58 70 7 77 65 30 0 0 11 1 0 1 30 41 31 40 0 7 2 0 16 0 1 0 0 0 0 0 0 0 C3 2011 REF 3 420 0.03 4517 100 0 0 0 100 7 177 12.5 8.4 10.6 537 704 95 52 Good 15 27 4.15 25 7 8 4 24 330 88 3 3 7 1 8 5 85 1 3 2 5 4 9 89 86 89 191 6 11 21 0 12 0 3 0 0 2 1 0 4 1 EC1 2011 REF 3 10 0.02 3915 93 2 0 5 96 5 167 16.0 8.2 10.1 740 895 80 41 Fair 15 15 5.74 22 8 6 39 15 375 56 3 35 35 4 39 39 54 1 2 0 5 3 8 57 55 60 123 8 5 3 3 9 0 0 0 1 3 1 0 0 2 GAV1 2011 MOD DIST 3 25 0.01 12791 59 0 0 41 79 4 140 19.9 8.2 5.9 1255 1554 77 24 Poor 7 5 6.52 15 7 3 57 5 292 38 0 55 59 1 60 57 35 0 2 3 5 2 7 37 38 40 94 3 0 0 2 1 0 4 0 0 0 0 0 5 0 M1 2011 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 5 92 24.6 8.3 12.6 1232 1243 65 6 Very Poor 1 0 6.80 8 1 0 64 0 971 35 0 52 62 3 65 55 38 0 0 9 1 0 1 38 47 39 104 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2011 HIGH DIST 1 50 0.02 643 24 76 0 0 24 3 106 18.9 7.9 9.3 1278 1448 95 16 Poor 2 3 6.36 8 2 5 54 5 1000 40 0 37 55 3 58 40 36 2 0 15 2 2 4 38 52 39 105 0 0 0 0 0 0 0 0 0 0 0 0 0 14 M3 2011 MOD DIST 3 400 0.07 4142 79 18 2 0 79 6 154 17.8 nm 10.2 834 966 83 34 Fair 6 9 5.73 16 9 14 38 14 1000 55 4 31 39 1 40 32 44 1 5 15 4 6 10 50 59 47 124 0 0 0 0 0 0 5 0 0 0 0 0 21 0 M4 2011 REF 2 1000 0.08 1376 98 2 0 0 98 7 173 14.1 8.3 9.8 563 713 99 47 Good 8 23 5.13 17 17 16 33 20 1000 62 2 32 35 1 36 33 48 1 12 2 5 13 17 60 49 52 126 0 0 0 0 13 0 18 0 1 1 0 0 0 0 SJ2 2011 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 5 101 14.7 8.2 6.7 1128 1406 81 30 Fair 9 9 6.72 19 10 8 72 9 493 22 4 62 72 1 73 63 17 0 5 10 5 5 10 22 27 22 39 2 1 0 0 1 0 9 0 0 0 0 0 6 1 SY1 2011 HIGH DIST 3 30 0.01 2482 45 54 2 0 45 4 109 13.6 8.2 10.4 2054 2620 97 28 Poor 5 1 6.10 12 10 9 38 9 660 51 8 35 40 1 41 36 44 0 0 11 9 1 10 45 55 53 124 0 0 0 0 0 0 0 0 0 0 1 0 2 0 SY2 2011 MOD DIST 3 170 0.03 1956 52 46 2 0 52 5 120 14.4 8.1 11.2 1698 2130 82 29 Fair 6 1 5.62 14 8 3 22 4 541 69 6 20 22 2 24 22 67 1 0 3 8 1 8 67 70 74 195 1 0 0 0 1 0 0 0 0 0 0 0 4 3 AB1 2012 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 5 107 14.5 8.1 7.9 1976 2473 92 7 Poor 2 2 7.14 8 2 2 74 2 733 23 0 10 13 63 76 73 84 0 0 4 2 0 2 84 88 86 63 0 0 0 0 0 0 0 0 0 0 0 0 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-4 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Value 5 2 1 0 2 2 0 0 0 2 3 3 1 5 5 S(0-3), M(4-6), T(7-10) M S S S S S S S S S S S S M M Primary FFG cg cg cg cg cg cg p sh p p NA sc sc cf ph Study Reaches Year Disturbance Group Order (ft.) Elevation Gradient watershed area % wilderness % urban % agriculture % herbaceous % undisturbed (ft) width Wet Habitat Score Stream temp. (c) pH Dissolved oxygen (mg/l) Conductivity (microS) Specific cond. (microS @ 25 c) % riparian canopy cover Updated IBI Score Class. of Integrity Core Metrics # EPT families % sens BMIs Tolerance Value Avg. # insect families % sh+pred % PT BMIs tol % Other BMI Metrics %EPT - Baetidae BMI density (#/sq. m) % EPT % Coleoptera % chironomidae % diptera % non-insects % non-insects diptera + % non-insects+chironimidae % cg %sc %sh % cf % pred %sc+sh %sc+sh+pred %cg+sc+sh %cg+cf %cg+pred Individual BMI Taxa Baetidae Caenidae Emphemerellidae Heptagenidae Leptohyphidae Leptophlebiidae Chloroperlidae Nemouridae Perlidae Perlodidae Brachycentridae Glossostomatidae Helicopsychidae Hydropsychidae Hydroptilidae AB3 2012 MOD DIST 2 300 0.03 2356 90 3 6 0 90 5 150 14.9 8.6 10.1 952 1180 62 40 Fair 9 38 4.90 18 5 9 30 9 1320 23 3 7 41 33 73 40 68 11 1 4 3 12 15 80 73 72 42 1 0 0 0 1 0 0 0 0 12 0 0 9 1 AB5 2012 HIGH DIST 1 10 0.02 275 30 70 0 0 30 2 117 14.7 7.7 5.9 2769 3446 100 14 Poor 2 1 6.84 11 8 2 59 2 330 5 3 27 31 55 85 82 57 2 0 4 7 2 10 59 61 64 10 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2012 REF 2 150 0.04 2583 100 0 0 0 100 5 175 13.7 8.6 10.3 777 991 100 65 Excellent 16 57 3.89 24 29 39 21 55 600 70 1 21 25 2 27 23 33 7 22 4 6 29 35 62 37 39 45 8 0 10 12 16 3 2 1 0 15 7 6 11 0 C1 2012 MOD DIST 4 15 0.01 9598 80 3 17 0 80 6 115 17.1 7.9 8.9 1275 1503 60 2 Very Poor 0 1 8.09 7 1 0 83 0 733 0 0 11 12 87 99 98 70 15 0 2 1 15 16 86 72 71 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2012 REF 3 420 0.03 4517 100 0 0 0 100 7 167 14.9 8.6 9.0 553 685 100 51 Good 10 50 4.82 19 19 17 44 40 240 43 6 42 46 3 50 46 35 1 15 2 4 16 20 51 37 39 8 42 0 1 2 10 0 0 0 0 0 1 2 0 0 GAV1 2012 MOD DIST 3 25 0.01 12791 59 0 0 41 79 4 140 18.5 8.1 7.2 1439 1643 80 49 Good 8 63 3.35 17 9 6 8 59 174 78 2 4 5 13 18 17 85 1 5 1 4 6 10 91 85 89 30 49 0 0 34 9 0 0 0 0 0 0 0 0 1 M1 2012 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 6 111 24.6 8.5 13.4 1283 1294 70 17 Poor 2 1 6.12 10 1 3 37 3 330 60 0 29 33 6 39 35 64 0 0 2 1 0 1 64 66 65 171 0 0 0 0 0 0 0 0 0 0 0 0 0 10 M3 2012 MOD DIST 3 400 0.07 4142 79 18 2 0 79 5 167 14.7 8.7 10.1 902 1123 95 52 Good 12 27 4.85 25 17 14 28 17 375 55 5 13 24 12 35 25 55 6 9 7 8 14 23 69 62 63 112 4 1 2 0 3 0 7 0 0 0 5 0 0 4 M4 2012 REF 2 1000 0.08 1376 98 2 0 0 98 4 168 13.3 8.7 10.1 640 822 98 56 Good 11 47 4.51 19 27 26 37 44 1000 54 3 32 32 8 40 40 36 3 20 1 7 22 30 58 37 44 32 15 1 6 0 31 0 10 0 0 4 1 0 2 0 R0 2012 MOD DIST 3 180 0.02 3700 78 8 10 4 80 4 160 14.4 8.7 9.4 1483 1860 90 56 Good 15 31 4.94 26 13 19 30 33 559 60 1 25 34 3 37 29 45 5 7 9 6 12 18 57 54 51 83 36 0 2 0 5 0 8 0 1 5 5 0 5 0 SJ2 2012 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 4 122 18.7 8.0 7.5 1457 1657 70 46 Good 8 53 4.08 17 13 9 27 37 150 38 12 15 19 27 47 43 53 16 4 1 9 20 29 73 53 62 2 9 0 0 32 0 0 0 0 0 3 4 0 0 0 SY1 2012 HIGH DIST 3 30 0.01 2482 45 53 2 0 45 4 115 15.4 8.9 11.6 1526 1871 92 26 Poor 5 4 6.28 13 8 7 48 7 330 35 2 34 41 21 62 55 37 9 0 11 7 9 17 47 48 45 82 0 0 0 0 0 0 0 0 0 0 0 0 3 0 SY2 2012 MOD DIST 3 170 0.03 1956 52 46 2 0 52 5 129 15.3 8.8 10.6 1339 1645 93 29 Fair 8 4 6.37 19 7 9 51 10 375 41 2 36 47 8 55 44 39 2 1 16 6 3 9 42 54 45 92 1 0 0 0 1 0 0 0 0 0 2 0 14 0 AB1 2013 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 5 119 19.6 7.9 9.5 1706 1902 80 25 Poor 6 4 7.07 15 8 15 76 15 1384 18 2 32 44 33 78 65 37 1 1 22 5 2 7 38 59 42 13 0 0 0 0 0 0 0 0 0 5 1 0 6 0 AB3 2013 MOD DIST 2 300 0.03 2356 90 3 6 0 90 3 116 15.4 7.4 3.6 1831 2240 77 13 Poor 5 2 7.16 11 6 0 82 1 440 3 3 49 50 43 93 91 37 8 0 0 6 8 14 45 37 43 6 0 0 0 0 1 0 0 0 0 0 0 0 0 0 AB5 2013 HIGH DIST 1 10 0.02 275 30 70 0 0 30 2 113 16.3 7.4 7.2 3431 4112 100 10 Very Poor 2 0 7.07 13 6 1 73 1 330 2 3 41 48 44 91 85 28 17 0 5 7 17 24 45 33 34 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2013 REF 2 150 0.04 2583 100 0 0 0 100 3 153 14.7 7.6 8.4 1099 100 65 Excellent 16 55 4.13 32 18 21 29 43 600 47 1 27 36 4 40 31 34 8 8 6 9 16 26 50 40 43 11 30 0 4 26 8 1 8 1 0 0 2 2 11 1 C1 2013 MOD DIST 4 15 0.01 9598 80 3 17 0 80 5 94 15.8 7.6 6.2 1568 75 2 Very Poor 1 2 7.88 3 1 0 81 0 173 1 0 21 23 76 99 98 57 15 0 4 1 15 16 72 61 58 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2013 REF 3 420 0.03 4517 100 0 0 0 100 5 144 13.0 7.9 9.0 795 89 46 Good 9 36 5.40 22 17 13 53 33 398 38 3 45 53 3 56 48 28 2 11 7 6 13 19 41 35 34 15 48 5 0 7 0 0 0 0 0 0 0 1 1 0 GAV1 2013 MOD DIST 3 25 0.01 12791 59 0 0 41 79 3 122 14.6 7.5 8.1 2029 58 54 Good 9 55 4.17 16 27 17 35 50 1065 52 0 24 26 15 41 39 47 0 15 2 12 15 27 62 48 58 4 53 0 0 45 3 0 28 0 0 3 0 0 0 0 M1 2013 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 5 93 23.3 7.7 9.0 1423 1471 67 3 Very Poor 2 0 7.76 5 4 0 93 0 750 3 0 78 84 13 97 91 12 0 0 6 4 0 4 12 18 16 8 0 0 0 0 0 0 0 0 0 1 0 0 0 0 M2 2013 HIGH DIST 1 50 0.02 643 24 76 0 0 24 3 111 18.5 8.0 9.5 1274 1454 95 9 Very Poor 1 4 6.05 5 7 2 40 2 1065 2 0 35 39 52 91 87 5 47 0 0 7 47 54 52 5 12 0 0 0 0 0 0 0 0 0 0 0 0 0 0 6 M3 2013 MOD DIST 3 400 0.07 4142 79 18 2 0 79 4 148 15.6 7.6 6.3 991 1209 95 32 Fair 9 18 6.07 17 11 5 69 12 440 12 6 27 31 49 80 76 56 3 1 1 11 4 15 60 57 67 1 6 0 2 0 13 0 2 0 0 1 2 0 2 0 M4 2013 REF 2 1000 0.08 1376 98 2 0 0 98 4 165 15.4 7.9 9.1 797 976 93 43 Fair 12 33 5.61 26 12 9 58 28 750 29 2 49 54 9 62 58 30 4 4 2 10 8 18 38 32 40 1 27 4 2 0 25 0 4 0 0 0 6 0 2 0 SA2 2013 MOD DIST 3 500 0.05 2556 94 0 2 4 96 3 123 19.2 7.5 7.0 1623 93 32 Fair 6 31 5.17 16 12 1 38 26 213 30 2 27 31 28 59 55 41 19 1 0 11 20 31 61 41 52 7 2 0 1 0 50 0 0 0 0 1 0 0 0 0 SJ2 2013 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 2 110 17.6 7.5 9.0 2360 77 45 Fair 8 37 5.57 16 25 23 56 32 166 33 4 31 36 26 62 57 39 3 21 1 4 24 28 63 39 43 1 4 0 0 10 0 0 1 0 0 0 2 0 1 0 SY1 2013 HIGH DIST 3 30 0.01 2482 45 53 2 0 45 2 92 16.1 8.0 7.3 2463 2969 98 20 Poor 5 4 5.43 11 9 5 23 5 660 7 2 6 6 83 89 89 18 62 1 4 7 63 70 81 22 25 4 0 0 0 0 0 0 0 0 0 1 0 0 11 0 SY2 2013 MOD DIST 3 170 0.03 1956 52 46 2 0 52 4 127 16.2 7.6 8.0 1762 2121 95 31 Fair 5 11 6.52 15 15 17 62 17 750 19 2 51 56 16 72 66 13 6 4 12 10 10 21 23 25 23 7 0 0 0 0 0 0 0 0 0 6 0 0 30 0 AB1 2014 HIGH DIST 3 25 0.01 5646 51 38 7 4 53 5 122 17.9 7.9 10.8 1646 72 15 Poor 4 1 6.99 11 2 5 69 5 1205 25 0 51 55 18 74 70 32 4 0 9 2 4 6 36 42 34 55 0 0 0 0 0 0 0 0 0 0 1 0 13 0 AB3 2014 MOD DIST 2 300 0.03 2356 90 3 6 0 90 5 154 15.3 7.8 8.2 1934 77 12 Poor 2 3 7.04 11 8 1 85 1 185 5 4 36 79 11 90 47 12 2 0 41 8 2 10 14 53 21 8 0 0 0 0 0 0 0 0 0 0 0 0 0 1 AB5 2014 HIGH DIST 1 10 0.02 275 30 70 0 0 30 2 109 15.4 7.2 6.1 3371 100 4 Very Poor 1 0 6.78 5 4 0 71 0 255 0 3 31 32 64 96 95 52 12 0 1 4 12 16 64 53 56 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2014 REF 2 150 0.04 2583 100 0 0 0 100 3 174 12.8 8.1 9.7 1246 94 47 Good 14 27 5.57 23 13 19 52 34 901 39 2 45 54 1 55 46 23 2 4 17 9 6 15 29 40 32 17 28 0 2 3 13 5 5 2 3 0 0 0 0 3 C1 2014 MOD DIST 4 15 0.01 9598 80 3 17 0 80 3 129 15.6 7.5 6.5 1835 85 7 Very Poor 0 2 6.78 6 6 0 74 0 241 0 0 17 18 78 97 95 54 21 0 2 5 21 26 75 56 59 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2014 REF 3 420 0.03 4517 100 0 0 0 100 5 165 13.3 7.9 9.1 1000 99 24 Poor 11 14 6.36 18 3 3 75 14 390 22 2 31 73 3 76 34 22 1 1 42 3 1 4 23 64 25 23 1 1 3 0 28 0 2 0 2 0 0 1 1 1 GAV1 2014 MOD DIST 3 25 0.01 12791 59 0 0 41 79 2 144 14.1 7.5 7.3 2778 62 14 Poor 4 5 6.98 11 8 1 72 2 206 6 5 66 68 20 88 86 19 6 0 0 8 6 15 25 19 27 9 0 0 0 0 2 0 0 0 1 1 0 0 0 0 M1 2014 HIGH DIST 3 40 0.01 6799 49 49 2 0 49 3 95 18.6 7.7 11.2 1433 55 3 Very Poor 0 0 7.74 3 6 0 93 0 159 0 0 64 69 31 100 95 25 0 0 5 6 0 6 25 30 31 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2014 HIGH DIST 1 50 0.02 643 24 76 0 0 24 2 122 19.3 8.1 9.3 1465 95 3 Very Poor 0 0 7.52 4 7 0 85 0 300 0 0 77 82 13 95 90 3 9 0 4 6 9 16 13 7 10 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M3 2014 MOD DIST 3 400 0.07 4142 79 18 2 0 79 4 155 15.9 7.8 8.5 1280 85 27 Poor 8 15 6.55 20 10 3 75 12 319 12 4 44 55 24 79 68 29 3 2 13 8 5 13 34 42 37 2 14 0 1 0 11 0 0 0 0 0 0 0 0 0 M4 2014 REF 2 1000 0.08 1376 98 2 0 0 98 4 169 16.8 7.7 6.3 953 100 28 Poor 7 16 6.22 22 11 2 72 13 400 15 3 24 46 31 77 54 42 2 2 21 9 4 13 46 62 51 7 17 1 0 0 15 0 4 0 0 0 0 0 0 0 SJ2 2014 HIGH DIST 3 120 0.01 3836 81 1 16 1 82 4 130 16.9 7.8 9.4 2228 93 26 Poor 10 6 6.94 22 6 7 75 9 938 18 0 47 75 3 78 50 23 2 1 21 5 3 8 26 44 28 29 3 0 0 0 1 0 1 0 0 1 4 0 5 0 SY2 2014 MOD DIST 3 170 0.03 1956 52 46 2 0 52 5 129 14.7 7.7 8.2 2618 83 25 Poor 7 5 6.65 15 13 4 67 6 800 18 1 45 62 11 73 56 22 3 1 17 12 4 16 26 39 35 36 3 0 0 0 2 0 0 0 0 0 0 0 7 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-5 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Va 2 4 4 0 5 2 5 2 3 4 5 5 0 5 9 5 2 0 5 8 8 3 4 6 6 6 5 6 7 3 1 8 8 5 5 3 3 5 5 3 0 5 9 0 3 10 3 7 7 7 9 8 5 9 9 10 4 NA NA NA NA NA NA NA NA S(0-3), M(4-6), TS M M S M S M S S M M M S M T M S S M T T S M M M M M M T S S T T M M S S M M S S M T S S T S T T T T T M T T T M NA NA NA NA NA NA NA NA Primary FFGsh om s sh cf p sc p sh p sh p cg p s p sc sc p NA cg cg p p NA p cg p cf cg NA p p p p NA p p p p p p p p p cg p sc cg cg cg sh cg cg cg pa p cg NA p NA pa NA NA cf Study Reaches Year Lepidostomatidae Leptoceridae Limnophilidae Odontoceridae Philopotamidae Polycentropodidae Psychomyiidae Rhyacophilidae Sericostomatidae Carabidae Dryopidae Dytiscidae Elmidae Gyrinidae Halipidae Hydrophilidae Psphenidae Blephariceridae Ceratopogonidae Chironomidae Culicidae Dixidae Dolichopodidae Empididae Ephydridae Muscidae Psychodidae Sciomyzidae Simulidae Stratiomyidae Tipulidae Belostomatidae Corixidae Gerridae Naucoridae Veliidae Aeshnidae Calypterygidae Coenagrionidae Cordulegastridae Gomphidae Lestidae Libellulidae Corydalidae Sialidae COLLEMBOLA ACARI GASTROPODA OSTRACODA COPEPODA CLADOCERA DECAPODA AMPHIPODA ISOPODA OLIGOCHAETA HIRUDINEA TURBELLARIA Others-no tolerance values Chrysomelidae Hydraenidae Notonectidae LEPIDOPTERA HYMENOPTERA NEMATOMORPHA NEMATODA BIVALIA (CLAM) AB2 2000 0 0 0 0 0 0 0 0 0 0 0 3 0 1 3 2 0 0 1 90 0 0 0 0 0 1 0 0 1 1 2 0 0 0 0 0 0 0 13 0 0 1 0 0 0 0 3 41 40 4 0 0 0 0 6 2 0 0 0 0 0 0 0 0 0 AB3 2000 11 0 0 0 1 2 1 1 10 0 0 5 4 0 2 0 0 0 0 54 0 0 0 0 0 1 0 0 4 10 1 2 0 0 0 0 5 0 1 0 0 1 0 2 0 0 4 21 1 0 0 0 0 0 9 0 0 0 0 0 0 0 0 0 0 AH1 2000 34 0 0 0 0 0 0 3 9 0 0 0 16 0 0 0 16 0 1 48 0 2 0 0 0 0 5 0 5 1 8 0 0 0 0 1 0 0 1 2 0 0 0 0 2 0 7 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH2 2000 7 0 0 0 0 0 0 3 1 0 0 1 31 0 0 0 8 0 1 33 0 0 0 0 0 0 2 0 54 3 2 0 0 0 0 2 0 0 2 0 0 0 0 1 0 0 2 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C1 2000 0 0 0 0 0 0 0 0 0 0 0 7 0 1 8 0 0 0 21 160 0 0 0 1 2 2 0 0 36 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 7 39 6 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 C2 2000 0 0 0 0 0 0 0 0 0 0 0 39 1 0 5 1 0 0 6 16 0 0 0 0 1 0 0 0 52 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 1 1 4 3 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2000 6 0 0 0 0 0 0 8 0 0 0 31 63 0 1 0 0 0 1 7 0 0 0 0 0 0 2 0 0 49 0 5 0 0 0 0 0 0 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 DP1 2000 0 1 0 0 3 0 0 0 0 0 0 1 2 0 0 0 1 0 0 28 0 0 0 0 0 0 0 0 6 2 1 1 1 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 50 1 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 F1 2000 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 138 0 0 0 0 2 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 3 0 0 154 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 M1 2000 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 55 0 0 0 0 0 0 0 0 1 1 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 1 41 110 80 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M3 2000 10 1 0 0 0 3 2 5 29 0 0 6 11 0 11 0 4 0 3 63 0 0 0 0 0 0 0 0 21 4 4 1 0 0 0 1 0 0 0 1 0 0 0 1 1 0 4 1 3 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 M4 2000 12 0 0 0 0 3 1 6 1 0 0 0 33 0 0 0 18 0 1 35 0 0 0 0 0 0 1 0 0 15 4 0 0 0 0 0 1 0 4 5 7 0 0 0 3 0 3 3 10 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 MY1 2000 0 0 0 0 0 0 0 0 0 0 0 1 8 1 1 0 0 0 0 31 0 0 0 0 0 0 0 0 8 5 1 1 1 0 4 1 0 0 2 0 0 2 1 0 5 0 2 17 0 0 0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 MY2 2000 0 0 0 0 1 0 0 6 12 0 4 18 53 0 1 0 1 0 1 20 0 0 0 0 0 0 0 0 13 40 0 1 0 0 0 1 1 0 6 0 0 1 0 0 9 0 3 0 0 0 0 0 0 0 4 0 0 0 0 2 0 0 0 0 0 MY3 2000 10 0 0 0 0 9 0 4 2 0 0 13 7 0 4 0 19 0 1 95 0 0 0 2 0 0 2 0 1 0 3 0 3 0 0 2 0 0 0 5 0 4 0 6 2 0 3 2 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 R1 2000 1 0 0 0 1 1 5 0 0 0 1 1 0 0 0 0 1 0 0 73 0 0 0 0 0 0 2 0 0 6 1 2 0 0 0 4 0 0 8 1 0 0 0 0 0 0 2 4 9 0 0 0 0 0 4 0 0 0 0 0 0 0 1 0 0 R2 2000 7 0 0 0 3 2 3 5 12 0 3 4 11 0 1 0 45 0 0 28 0 0 0 0 0 0 2 0 1 29 3 3 3 0 0 2 0 0 0 1 0 4 0 2 1 0 4 0 1 0 0 0 0 0 5 0 0 0 0 1 0 0 0 0 0 SA1 2000 0 0 0 0 3 1 1 0 1 0 0 14 3 0 9 0 0 0 1 45 0 2 0 0 0 0 1 0 1 24 0 3 2 1 0 0 0 0 0 0 0 2 0 0 2 0 0 13 34 0 0 0 0 0 2 0 0 0 0 5 0 0 0 0 0 SA2 2000 1 0 0 0 2 3 6 6 3 0 1 7 42 1 3 0 6 0 1 17 0 0 0 0 0 0 1 0 1 63 1 3 0 0 0 2 0 0 6 1 0 4 0 0 2 0 2 2 13 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 SJ1 2000 0 0 0 0 0 0 0 0 0 0 0 6 1 0 9 0 0 0 0 132 0 0 0 0 0 0 0 0 46 2 0 0 4 0 3 0 0 0 1 0 0 0 0 0 0 0 2 3 9 0 0 0 0 0 15 1 0 0 0 0 0 0 0 0 0 SJ2 2000 0 0 1 0 2 0 0 0 0 0 0 1 29 0 4 0 0 0 2 59 0 0 0 0 0 0 0 0 12 5 0 0 0 0 0 0 0 0 2 1 0 0 0 0 1 0 5 0 4 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SJ3 2000 18 0 0 0 1 1 0 7 9 1 6 7 22 0 1 1 2 0 1 88 0 0 0 0 0 0 3 0 14 4 1 1 0 2 0 6 1 0 0 1 1 2 0 0 11 0 5 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SM1 2000 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 2 285 0 0 0 0 2 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 5 0 0 0 0 0 0 0 0 0 0 0 0 0 4 0 0 0 SO1 2000 3 0 0 0 0 1 0 0 0 0 0 6 1 0 0 0 7 0 2 20 0 3 0 0 0 0 3 0 16 0 1 0 7 0 0 0 0 0 3 2 0 0 0 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 5 0 0 0 SO2 2000 1 0 0 0 0 1 0 4 0 0 0 2 5 0 0 0 7 9 0 18 0 1 0 0 0 0 0 0 4 4 8 0 3 1 0 0 0 0 0 1 1 0 0 0 5 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 23 0 0 0 T1 2000 0 2 0 0 0 0 0 0 2 0 0 7 2 0 0 2 0 0 0 15 2 0 0 0 0 0 0 0 4 0 1 1 1 0 0 1 0 0 1 0 0 0 0 0 1 0 2 0 78 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 T2 2000 0 0 0 0 1 0 2 0 13 0 0 4 1 1 0 0 0 0 1 23 0 0 0 2 0 0 0 0 4 33 2 0 1 0 1 1 0 0 8 0 0 0 0 0 0 0 2 0 9 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB2 2001 0 0 0 0 0 0 0 0 0 0 0 15 0 0 10 0 0 0 1 182 0 0 0 0 0 0 0 0 42 1 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 2 0 0 18 0 0 0 6 0 0 0 0 0 0 1 0 0 0 AB3 2001 4 0 0 0 3 0 0 0 2 0 0 29 2 0 4 2 1 0 20 84 1 1 0 0 0 0 2 0 9 4 0 2 0 2 0 3 2 0 2 3 0 2 0 0 3 0 1 0 1 0 0 0 0 0 1 0 0 0 0 0 0 0 2 0 0 AH1 2001 3 0 0 0 0 1 0 1 0 0 0 3 12 0 0 0 5 0 14 140 0 3 1 0 0 0 2 0 11 0 12 0 0 0 0 2 0 0 0 0 0 0 0 0 2 0 7 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 AT1 2001 0 0 0 0 0 0 0 0 0 0 0 2 0 0 4 9 0 0 0 229 0 0 0 0 0 0 0 0 10 0 3 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 33 0 0 0 3 0 0 0 0 1 0 0 0 0 0 AT2 2001 0 0 0 0 0 0 0 0 0 0 0 6 0 0 0 5 0 0 6 178 0 0 0 0 0 1 25 0 16 5 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 3 4 0 0 13 0 0 0 2 1 0 0 0 0 0 0 0 0 0 C1 2001 0 0 0 0 0 0 0 0 0 0 0 5 1 0 1 0 0 0 3 244 0 0 0 0 0 0 1 0 20 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 4 14 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 C2 2001 0 0 0 0 0 0 0 0 0 0 0 13 0 1 2 0 0 0 4 191 1 0 0 0 1 0 0 0 44 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 17 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2001 1 0 0 0 3 2 1 5 0 0 0 9 25 0 0 0 0 0 5 81 0 1 0 0 0 0 2 0 11 16 4 1 0 0 0 0 2 0 0 2 0 0 2 1 3 0 2 0 1 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 SJ1 2001 0 0 0 0 0 0 0 0 0 0 0 11 4 0 3 0 0 0 3 178 0 1 0 0 0 1 0 0 39 2 4 2 0 0 0 1 0 0 0 0 0 0 1 1 0 0 2 2 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 SJ2 2001 0 0 0 0 1 0 0 1 1 0 0 8 2 0 1 0 1 0 1 140 0 1 1 0 1 0 0 0 87 0 2 2 0 0 0 1 0 0 0 0 0 0 0 0 0 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SJ3 2001 3 0 0 0 1 1 0 2 3 0 0 18 6 0 0 0 7 1 2 71 1 0 0 0 0 0 3 0 5 4 4 0 0 1 0 3 2 0 0 0 2 4 0 0 3 0 2 1 0 0 0 0 0 0 4 0 0 0 0 0 0 0 1 0 0 SO2 2001 7 0 0 0 0 1 0 7 0 0 0 0 5 0 0 0 20 4 0 37 0 5 0 0 0 0 0 0 21 0 16 0 1 0 0 2 0 0 0 1 0 1 1 2 0 0 2 0 1 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 AB1 2002 0 0 0 0 0 0 0 0 0 0 0 14 0 1 7 0 0 0 0 104 0 0 0 1 1 0 0 0 0 0 0 0 2 0 0 0 1 0 0 0 0 6 0 0 0 0 0 16 42 0 38 0 0 12 0 1 0 0 0 8 0 0 0 0 0 AB2 2002 0 0 0 0 0 0 0 0 0 0 0 7 0 2 1 0 0 0 9 83 0 0 0 0 7 0 4 0 30 3 2 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 2 7 13 43 79 0 0 0 0 1 0 0 0 0 0 0 0 0 0 AB3 2002 15 0 0 0 3 2 2 0 10 0 1 7 1 0 0 0 6 0 12 52 0 0 0 0 0 0 1 0 1 16 4 0 0 0 0 0 1 0 3 6 1 2 1 0 0 0 0 2 57 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 AH1 2002 16 2 0 0 0 3 0 0 13 0 0 2 3 0 0 0 9 0 8 75 0 1 0 0 0 0 6 0 0 3 20 0 0 0 0 2 0 0 1 0 0 1 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT1 2002 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 99 0 0 0 0 0 0 0 0 0 0 2 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 9 2 183 0 0 0 0 3 0 0 0 0 0 0 0 0 0 AT2 2002 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 6 0 0 0 262 0 0 0 0 0 0 1 0 1 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 1 0 6 11 0 2 0 0 2 0 0 0 0 0 0 0 0 0 0 C1 2002 0 0 0 0 0 0 0 0 0 0 0 5 0 0 1 2 0 0 3 96 0 0 0 0 4 0 2 0 19 5 3 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 21 33 14 38 0 0 0 51 0 0 0 0 0 0 0 0 0 0 C3 2002 12 1 0 0 3 0 1 8 5 0 0 2 22 0 0 0 0 0 1 32 0 2 0 0 0 0 2 0 0 4 4 0 0 0 0 0 0 0 0 6 0 0 5 0 0 0 0 0 5 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 EC1 2002 0 0 0 0 0 8 0 2 0 0 1 12 2 1 1 0 0 0 1 46 0 1 0 0 0 0 1 0 2 1 1 0 14 0 0 1 0 0 1 0 0 1 0 0 0 0 4 16 65 1 0 0 0 3 3 3 0 0 0 0 0 0 0 0 0 GAV1 2002 0 2 0 0 0 3 14 0 0 0 3 0 3 0 0 0 0 0 2 46 0 0 0 0 15 0 0 0 5 0 2 2 4 0 28 7 0 0 2 0 0 1 0 0 5 0 2 1 13 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 GAV2 2002 1 0 0 0 0 1 4 0 2 0 0 0 1 0 0 1 0 0 0 87 0 0 0 1 0 0 0 0 3 12 6 1 4 0 5 0 0 0 7 0 0 0 4 0 4 0 1 1 3 0 0 0 0 2 1 0 0 0 0 0 0 0 0 0 0 M1 2002 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 218 0 0 0 0 0 0 0 0 2 0 0 0 16 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 14 0 41 0 0 0 0 4 0 0 0 0 0 1 0 0 0 M2 2002 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 231 0 0 0 4 0 0 0 0 2 0 0 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 1 2 8 0 0 0 0 1 12 0 0 0 0 0 0 0 0 0 M3 2002 14 0 0 0 0 5 0 0 9 0 0 9 3 0 2 0 49 0 10 36 0 0 0 0 0 0 3 0 0 12 1 3 0 0 0 2 3 0 3 1 1 9 2 0 1 0 4 2 12 6 0 0 0 0 3 1 0 0 0 0 0 0 0 0 0 RIN1 2002 8 0 0 0 0 1 1 6 5 0 0 5 3 1 0 0 6 0 3 20 0 0 0 0 0 0 1 0 4 7 6 1 1 1 0 1 0 0 0 0 0 0 2 0 0 0 5 4 69 0 0 0 0 1 1 0 0 0 0 0 0 0 0 0 0 SJ1 2002 0 0 0 0 0 0 0 0 0 0 0 6 3 0 4 9 0 0 13 189 0 0 0 0 0 0 1 0 13 11 2 0 5 1 1 0 0 0 0 0 0 0 0 0 0 0 4 4 17 3 0 0 0 0 2 2 1 0 0 0 0 1 1 0 0 SJ2 2002 0 0 0 0 0 0 1 3 4 0 0 2 9 1 0 0 3 0 16 100 0 1 0 1 0 0 1 0 3 6 1 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 4 2 47 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 SJ3 2002 17 1 2 0 0 3 1 10 11 0 0 5 19 0 1 0 6 0 1 57 0 0 0 0 0 0 3 0 1 1 0 0 0 0 0 0 1 0 0 2 3 0 2 1 0 0 3 13 1 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 SO2 2002 30 1 0 0 0 3 0 7 11 0 0 0 2 0 0 0 30 0 6 63 0 1 0 0 0 0 5 0 0 2 7 1 1 0 0 0 0 0 3 4 6 0 0 0 0 0 1 1 2 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-6 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Va 2 4 4 0 5 2 5 2 3 4 5 5 0 5 9 5 2 0 5 8 8 3 4 6 6 6 5 6 7 3 1 8 8 5 5 3 3 5 5 3 0 5 9 0 3 10 3 7 7 7 9 8 5 9 9 10 4 NA NA NA NA NA NA NA NA S(0-3), M(4-6), TS M M S M S M S S M M M S M T M S S M T T S M M M M M M T S S T T M M S S M M S S M T S S T S T T T T T M T T T M NA NA NA NA NA NA NA NA Primary FFGsh om s sh cf p sc p sh p sh p cg p s p sc sc p NA cg cg p p NA p cg p cf cg NA p p p p NA p p p p p p p p p cg p sc cg cg cg sh cg cg cg pa p cg NA p NA pa NA NA cf Study Reaches Year Lepidostomatidae Leptoceridae Limnophilidae Odontoceridae Philopotamidae Polycentropodidae Psychomyiidae Rhyacophilidae Sericostomatidae Carabidae Dryopidae Dytiscidae Elmidae Gyrinidae Halipidae Hydrophilidae Psphenidae Blephariceridae Ceratopogonidae Chironomidae Culicidae Dixidae Dolichopodidae Empididae Ephydridae Muscidae Psychodidae Sciomyzidae Simulidae Stratiomyidae Tipulidae Belostomatidae Corixidae Gerridae Naucoridae Veliidae Aeshnidae Calypterygidae Coenagrionidae Cordulegastridae Gomphidae Lestidae Libellulidae Corydalidae Sialidae COLLEMBOLA ACARI GASTROPODA OSTRACODA COPEPODA CLADOCERA DECAPODA AMPHIPODA ISOPODA OLIGOCHAETA HIRUDINEA TURBELLARIA Others-no tolerance values Chrysomelidae Hydraenidae Notonectidae LEPIDOPTERA HYMENOPTERA NEMATOMORPHA NEMATODA BIVALIA (CLAM) SY1 2002 0 0 0 0 2 0 0 0 12 0 0 3 2 0 2 0 1 0 11 74 0 0 0 1 0 0 4 0 0 0 1 1 0 0 0 1 0 0 0 0 0 1 0 1 0 0 1 42 129 0 0 0 0 0 2 2 0 0 0 3 0 0 0 0 0 AB1 2003 0 0 0 0 0 0 0 0 0 0 0 8 0 0 2 0 0 0 0 29 0 0 0 1 0 0 0 0 36 0 2 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 3 4 53 2 2 0 0 38 2 2 2 0 0 0 0 0 0 0 0 AB2 2003 0 0 0 0 0 0 0 0 0 0 0 3 0 0 4 0 0 0 1 129 0 0 0 0 0 0 0 0 12 0 2 0 0 0 0 0 2 0 3 0 0 0 0 0 0 2 0 1 14 8 0 0 0 0 23 0 1 0 0 1 0 0 0 0 0 AB3 2003 2 0 0 0 1 0 0 0 0 0 0 11 1 0 1 0 0 0 7 59 0 2 0 0 1 0 0 0 54 2 0 0 0 1 0 1 2 0 0 3 0 0 0 1 2 0 1 10 16 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 AH1 2003 34 0 0 0 0 1 0 10 19 0 0 1 12 0 0 0 10 0 0 36 0 4 0 0 0 0 1 0 12 1 4 0 0 0 0 3 0 0 0 2 3 0 0 1 1 0 3 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT1 2003 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 30 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 11 5 5 246 0 0 0 2 1 0 0 0 0 0 0 0 0 0 AT2 2003 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 40 0 0 0 0 0 1 0 0 53 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 1 2 6 7 28 1 0 0 49 1 0 0 0 0 0 0 0 0 0 C1 2003 0 0 0 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 1 231 0 0 0 0 3 2 0 0 2 1 6 0 0 0 0 0 0 0 0 0 0 0 0 0 0 5 0 0 13 0 1 0 0 0 26 0 0 0 0 0 0 0 0 0 0 C3 2003 13 0 0 0 4 0 1 9 1 0 0 6 8 0 0 0 1 0 1 34 0 2 0 2 0 0 0 0 3 1 15 0 0 0 0 0 0 0 1 2 0 0 0 0 0 0 0 0 2 0 0 0 0 0 7 0 0 0 0 0 0 0 0 0 0 GAV1 2003 0 1 0 0 0 0 3 0 2 0 1 2 2 0 0 0 0 0 0 66 0 1 0 0 1 0 0 0 31 1 1 0 0 0 14 0 0 0 5 0 0 0 0 0 6 0 4 1 9 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 M1 2003 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 176 0 0 0 0 0 0 0 0 29 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 16 17 5 0 0 0 0 41 2 0 0 0 0 0 0 0 0 0 M2 2003 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 228 0 0 0 2 0 0 0 0 35 0 0 0 0 0 0 0 0 0 7 0 0 0 0 0 0 0 1 0 2 0 0 1 0 0 6 0 1 0 0 0 0 0 0 0 0 M3 2003 10 0 0 0 2 0 0 1 17 0 0 5 4 0 0 0 6 0 0 71 0 0 0 0 0 0 1 0 40 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 5 1 0 0 0 0 0 0 9 0 2 0 0 0 0 0 0 0 0 MONT1 2003 18 0 0 0 1 8 1 15 15 0 0 2 17 0 1 0 11 0 0 29 0 1 0 1 0 0 0 0 17 0 2 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 3 30 7 0 0 0 25 1 13 0 0 0 0 0 0 0 0 0 0 SA2 2003 4 0 0 0 0 1 0 0 3 0 0 24 7 0 3 0 0 1 1 36 0 2 0 0 0 2 0 0 0 4 2 1 1 0 0 0 0 0 2 1 0 0 0 0 0 0 3 2 5 0 0 0 0 0 2 0 2 0 0 1 0 0 0 0 0 SJ1 2003 0 0 0 0 0 0 0 0 0 0 0 2 1 0 1 0 0 0 6 161 0 0 0 1 2 0 0 0 11 0 0 0 1 0 0 0 1 0 1 0 0 0 0 0 0 0 2 2 3 0 0 0 0 0 15 0 0 0 0 0 0 0 0 0 0 SJ2 2003 1 0 0 0 0 0 0 0 2 0 0 3 3 0 1 0 2 0 7 118 0 0 0 0 0 1 0 0 20 0 2 0 0 0 0 0 0 0 2 1 0 0 0 1 0 0 1 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 SJ3 2003 8 0 0 0 0 1 0 14 1 0 0 13 17 0 0 0 1 2 1 62 0 0 0 1 0 0 2 0 51 0 4 0 0 1 0 2 1 0 1 1 2 1 0 0 0 0 5 3 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 SO2 2003 14 0 0 0 0 1 0 9 5 0 0 0 8 0 0 0 15 0 3 31 0 6 0 1 0 0 1 0 27 1 4 1 0 1 0 3 0 0 1 2 2 0 0 2 2 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SY1 2003 0 0 0 0 8 0 0 1 5 0 0 7 4 0 2 1 0 0 2 109 0 0 0 1 0 0 0 0 32 0 0 1 0 0 0 0 0 0 0 0 0 1 0 0 0 0 1 0 1 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 SY2 2003 0 0 0 0 0 0 1 1 3 0 0 4 3 0 0 0 0 0 7 71 0 0 0 1 1 0 0 0 42 1 0 0 0 0 0 1 0 0 0 1 0 0 0 0 0 0 1 2 1 0 0 0 0 0 5 0 0 0 0 0 0 0 0 0 0 AB1 2005 0 0 0 0 1 0 0 0 0 0 0 3 0 0 1 0 0 0 0 18 0 0 0 0 0 0 0 0 80 0 0 1 0 0 0 0 0 0 2 0 0 1 0 1 0 0 0 0 0 0 0 0 0 2 1 0 0 0 0 0 0 0 0 0 0 AB2 2005 0 0 0 0 2 0 0 0 0 0 0 1 0 0 3 0 0 0 0 37 0 0 0 0 0 0 0 0 92 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 0 2 1 0 0 0 0 1 0 0 0 0 0 AB3 2005 2 0 0 0 0 0 0 2 0 0 0 2 0 0 0 0 0 0 0 45 0 0 0 0 0 0 0 0 67 1 1 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AH1 2005 0 0 0 0 0 0 0 2 0 0 0 2 1 0 0 0 1 0 3 42 0 3 0 0 0 0 1 0 6 0 0 0 0 0 0 1 0 0 0 0 1 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT1 2005 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 38 0 0 0 0 0 0 0 0 11 0 5 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 94 0 0 0 0 0 0 0 0 0 0 AT2 2005 0 0 0 0 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 59 0 0 0 0 1 0 0 0 7 0 1 0 0 1 0 0 0 0 1 0 0 0 0 0 0 0 0 1 8 0 0 1 0 0 74 0 0 0 0 0 0 0 0 0 0 C1 2005 0 0 0 0 0 0 0 0 2 0 0 2 1 0 0 0 0 0 0 127 0 0 0 0 1 0 0 0 6 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2005 0 0 0 0 1 0 0 0 0 0 0 3 3 0 0 0 0 0 2 98 0 0 0 1 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 GAV1 2005 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 112 0 0 0 0 5 0 0 0 5 0 1 1 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M1 2005 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 187 0 0 0 0 0 0 0 0 21 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 M2 2005 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 32 0 0 0 0 0 0 0 0 91 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 1 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 M3 2005 4 0 0 0 1 0 0 2 1 0 0 6 0 0 0 0 0 0 0 56 0 0 0 0 0 1 0 0 51 0 0 0 0 0 0 1 0 0 0 0 0 9 0 0 1 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 MONT1 2005 0 0 0 0 0 0 0 1 0 0 0 2 0 0 0 0 1 0 1 90 0 1 0 0 0 0 0 0 1 0 1 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SA2 2005 0 0 0 0 1 0 0 0 1 0 0 12 1 0 1 0 1 1 0 66 0 1 0 0 0 0 0 0 2 0 1 0 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SJ1 2005 0 0 0 0 0 0 0 0 1 0 0 4 0 0 0 0 0 0 1 118 1 0 0 0 0 1 0 0 20 1 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 14 0 0 0 0 0 0 0 0 0 0 SJ2 2005 0 0 0 0 0 0 0 0 0 0 0 6 6 0 1 0 3 0 1 12 0 0 1 0 0 0 0 0 2 0 0 1 0 0 0 0 0 0 1 0 0 0 0 1 0 0 1 0 1 0 0 0 0 0 1 0 0 0 0 0 0 0 3 0 0 SJ3 2005 1 0 2 0 0 0 0 2 5 0 0 6 0 0 0 0 0 0 0 69 0 1 0 0 0 0 0 0 11 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 1 0 1 0 0 3 0 0 0 0 1 0 0 0 0 0 1 0 0 0 0 SY1 2005 0 0 0 0 0 0 0 0 0 0 0 12 4 0 3 0 0 0 0 75 1 0 0 0 0 0 0 0 29 0 3 1 0 0 0 0 0 0 0 1 0 1 0 0 0 0 1 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SY2 2005 0 0 0 0 0 0 0 0 0 0 0 7 0 0 3 0 0 0 0 24 0 0 0 0 0 0 0 0 55 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 AB1 2006 0 0 0 0 2 0 0 0 0 0 0 1 0 1 0 0 0 0 2 68 0 0 0 0 0 0 1 0 24 2 1 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 1 2 2 2 0 0 0 3 8 2 0 0 0 0 0 0 0 0 0 AB3 2006 8 0 0 0 0 0 0 0 12 0 0 2 1 0 3 0 0 0 2 52 0 0 0 0 0 0 0 0 1 3 0 0 0 0 0 0 7 0 5 0 0 1 0 0 0 0 0 5 1 0 0 0 0 0 5 0 0 0 0 0 0 0 0 0 0 AB4 2006 0 0 0 0 0 0 0 0 0 0 0 5 0 0 6 0 0 0 6 142 0 0 0 0 0 1 0 0 4 1 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 1 5 6 0 0 0 0 0 7 0 4 0 0 0 0 0 1 0 0 AH1 2006 26 0 0 0 0 4 0 2 36 0 0 1 2 0 0 0 1 0 0 40 0 0 0 0 0 0 1 0 1 1 24 0 0 0 0 1 0 0 2 0 1 0 1 0 0 0 1 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 AT1 2006 0 0 0 0 0 0 0 0 0 0 0 2 1 0 4 0 0 0 0 207 0 0 0 0 0 0 4 0 4 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 1 3 1 0 0 1 0 6 0 0 0 0 0 0 0 0 0 0 AT2 2006 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 2 0 0 2 76 0 0 0 0 1 0 1 0 70 1 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 1 4 4 4 0 2 0 0 6 0 0 0 0 0 0 0 0 0 0 C1 2006 0 0 0 0 0 0 0 0 0 0 0 11 0 0 6 0 0 0 0 134 0 0 0 2 1 1 0 0 19 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 6 2 0 0 0 0 4 0 0 0 0 0 0 0 0 0 0 C3 2006 10 0 0 0 7 0 0 9 2 0 0 11 3 0 0 0 1 0 1 19 0 0 0 0 0 0 0 0 2 10 8 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 3 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M1 2006 0 0 0 0 1 0 0 0 0 0 0 0 1 0 0 0 0 0 0 225 0 0 0 0 0 0 0 0 6 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 1 1 2 0 0 0 0 16 0 1 0 0 0 0 0 0 0 0 M2 2006 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 148 0 0 0 1 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 2 0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 M3 2006 3 0 0 0 1 5 0 5 6 0 0 1 5 0 1 0 1 4 0 35 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 1 0 0 0 0 0 1 0 1 0 0 0 0 4 0 0 0 0 0 0 0 0 0 0 M7 2006 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 131 0 0 0 1 0 0 0 0 1 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 2 3 0 1 0 0 20 0 0 0 0 0 0 0 1 0 0 MONT2 2006 4 0 0 0 0 1 0 3 1 0 0 15 0 0 0 0 1 0 2 145 0 0 0 0 1 0 4 0 0 5 0 0 0 1 0 0 0 0 0 1 0 1 0 0 0 2 2 2 2 2 0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 RIN1 2006 6 0 0 0 4 0 0 4 0 0 0 20 1 0 1 0 0 0 0 14 0 0 0 0 0 0 0 0 45 8 2 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SA2 2006 1 0 0 0 2 0 0 1 2 0 0 4 0 1 0 0 0 0 2 36 0 0 0 0 0 0 0 0 1 6 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 SJ1 2006 0 0 0 0 0 0 0 0 0 0 0 8 4 2 3 0 0 0 8 170 0 0 0 1 0 0 1 0 3 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 11 1 2 0 0 0 0 0 19 0 0 0 0 0 0 0 0 0 0 SJ2 2006 0 0 0 0 0 0 0 2 1 0 0 6 12 1 1 0 2 0 2 97 0 0 0 1 2 0 0 0 20 0 1 2 0 0 0 0 1 0 2 0 0 0 0 0 1 0 6 0 1 0 0 0 0 0 3 0 0 0 0 0 0 0 1 0 0 SJ3 2006 4 0 0 0 0 2 0 7 2 0 0 4 18 0 0 0 0 4 2 53 0 0 0 0 0 0 2 0 8 3 4 0 0 0 0 0 4 0 1 0 2 5 0 0 0 0 0 1 0 1 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-7 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Va 2 4 4 0 5 2 5 2 3 4 5 5 0 5 9 5 2 0 5 8 8 3 4 6 6 6 5 6 7 3 1 8 8 5 5 3 3 5 5 3 0 5 9 0 3 10 3 7 7 7 9 8 5 9 9 10 4 NA NA NA NA NA NA NA NA S(0-3), M(4-6), TS M M S M S M S S M M M S M T M S S M T T S M M M M M M T S S T T M M S S M M S S M T S S T S T T T T T M T T T M NA NA NA NA NA NA NA NA Primary FFGsh om s sh cf p sc p sh p sh p cg p s p sc sc p NA cg cg p p NA p cg p cf cg NA p p p p NA p p p p p p p p p cg p sc cg cg cg sh cg cg cg pa p cg NA p NA pa NA NA cf Study Reaches Year Lepidostomatidae Leptoceridae Limnophilidae Odontoceridae Philopotamidae Polycentropodidae Psychomyiidae Rhyacophilidae Sericostomatidae Carabidae Dryopidae Dytiscidae Elmidae Gyrinidae Halipidae Hydrophilidae Psphenidae Blephariceridae Ceratopogonidae Chironomidae Culicidae Dixidae Dolichopodidae Empididae Ephydridae Muscidae Psychodidae Sciomyzidae Simulidae Stratiomyidae Tipulidae Belostomatidae Corixidae Gerridae Naucoridae Veliidae Aeshnidae Calypterygidae Coenagrionidae Cordulegastridae Gomphidae Lestidae Libellulidae Corydalidae Sialidae COLLEMBOLA ACARI GASTROPODA OSTRACODA COPEPODA CLADOCERA DECAPODA AMPHIPODA ISOPODA OLIGOCHAETA HIRUDINEA TURBELLARIA Others-no tolerance values Chrysomelidae Hydraenidae Notonectidae LEPIDOPTERA HYMENOPTERA NEMATOMORPHA NEMATODA BIVALIA (CLAM) SY1 2006 0 0 0 0 2 0 0 0 3 0 0 6 0 0 0 0 1 0 4 28 0 0 0 0 0 0 1 0 7 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 2 0 4 0 0 0 0 1 0 0 0 0 0 1 0 0 0 0 SY2 2006 0 0 0 0 15 0 0 0 0 0 0 9 0 0 0 0 1 0 1 49 0 0 0 0 3 0 1 0 21 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 2 1 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 T2 2006 0 0 0 0 6 0 0 0 0 0 0 51 0 0 9 1 0 0 0 62 0 0 1 1 0 0 0 0 21 0 0 0 1 0 0 0 1 0 0 1 0 0 0 0 3 0 6 0 6 0 0 0 0 0 6 0 0 0 0 0 0 0 0 0 0 AB1 2007 0 0 0 0 2 0 0 0 0 0 0 2 0 0 2 0 0 0 3 48 0 0 0 0 0 0 1 0 51 1 3 0 0 0 0 0 3 0 2 0 0 1 0 0 0 0 1 1 13 23 5 0 0 12 4 0 0 0 0 0 0 0 0 0 0 AB3 2007 2 0 0 0 7 0 1 0 1 0 0 9 0 0 0 0 0 0 7 73 0 0 0 0 0 0 1 0 12 0 1 0 0 0 0 0 8 0 5 1 0 4 0 0 0 1 0 18 141 0 0 0 0 0 3 0 0 0 0 1 0 0 0 0 0 AB4 2007 0 0 0 0 0 0 0 0 0 0 0 0 0 0 6 0 0 0 0 60 0 0 0 0 0 0 0 0 1 1 3 0 0 0 0 0 4 0 0 0 0 1 0 0 0 0 0 9 22 58 116 0 0 0 12 2 1 0 0 0 3 0 0 0 0 AB5 2007 0 0 0 0 0 0 0 0 0 0 0 5 0 0 0 0 0 0 1 98 0 0 0 0 0 2 1 0 12 0 1 0 0 1 0 0 2 0 5 0 0 0 0 0 0 0 0 1 56 2 0 0 16 22 8 0 0 0 0 0 0 0 0 0 0 AH1 2007 9 0 0 0 0 1 0 1 3 0 0 0 5 0 0 0 11 0 8 96 0 0 0 0 0 0 0 0 1 0 6 1 0 0 0 0 2 0 2 0 1 0 0 1 0 0 36 3 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 1 0 AT1 2007 0 0 0 0 0 0 0 0 0 0 0 1 0 0 8 1 0 0 1 71 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 1 0 1 0 0 0 0 0 0 0 1 7 78 45 61 0 1 0 20 2 0 0 0 0 0 0 0 0 0 AT2 2007 0 0 0 0 0 0 0 0 0 0 0 2 0 0 1 0 0 0 2 87 1 0 0 0 2 0 1 1 19 1 3 0 0 0 0 0 4 0 1 0 0 0 0 0 0 0 4 16 73 5 4 0 0 0 19 0 1 0 0 0 0 0 0 3 0 C1 2007 0 0 0 0 0 0 0 0 0 0 0 2 0 0 14 0 0 0 0 33 0 0 0 0 2 0 2 0 1 0 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 8 106 30 49 0 0 0 39 0 6 0 0 0 0 0 0 0 0 C3 2007 12 0 0 0 3 1 3 3 7 0 1 4 16 0 1 0 3 0 3 20 0 2 0 0 0 0 0 0 0 11 2 0 0 0 0 1 1 0 0 0 0 1 1 0 1 0 21 5 7 0 0 0 0 0 14 0 0 0 0 0 0 0 0 0 0 GAV1 2007 0 0 0 0 5 1 7 0 0 0 0 0 9 0 3 0 0 0 0 38 0 0 0 0 0 0 0 0 2 0 1 2 0 0 14 1 0 0 4 0 0 0 2 0 0 0 0 1 2 0 0 0 9 0 3 1 0 0 0 0 0 0 0 0 0 GAV1 2007 0 2 0 0 3 0 6 0 8 0 0 0 0 0 1 0 0 0 1 65 1 2 0 0 0 0 0 0 3 0 0 1 0 0 4 0 0 6 5 0 0 0 1 0 0 0 6 6 23 2 0 0 13 0 8 0 0 0 0 0 0 0 0 2 0 M1 2007 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 175 0 0 0 0 0 0 0 0 21 4 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 4 8 2 5 1 0 0 19 0 2 0 0 0 0 0 0 0 0 M2 2007 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 165 0 0 0 0 1 0 2 0 35 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 7 7 0 3 0 0 20 0 0 0 0 0 0 0 0 0 0 M3 2007 6 0 0 0 0 6 0 4 8 0 0 2 16 0 0 0 15 0 2 67 0 3 0 0 0 0 0 0 1 4 2 0 0 0 0 0 1 0 0 1 0 4 0 0 0 0 0 2 52 7 0 0 0 0 11 0 1 0 0 0 1 0 0 0 0 M4 2007 49 0 0 0 0 5 1 5 7 0 0 0 28 0 0 0 5 0 3 82 0 0 0 0 0 0 5 0 3 2 1 0 0 0 0 3 0 0 4 4 3 0 0 0 0 0 2 4 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M7 2007 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 98 0 0 0 0 0 0 0 0 57 0 1 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 1 1 2 0 1 0 0 13 0 0 0 0 0 0 0 0 0 0 MONT2 2007 1 0 0 0 0 3 0 0 0 0 0 9 3 0 0 0 2 0 1 18 0 0 0 0 0 1 0 0 1 9 0 0 0 0 0 0 0 0 1 1 0 0 1 0 0 0 21 75 110 11 0 0 0 0 21 0 0 0 0 0 0 0 0 3 0 RIN1 2007 2 0 0 0 3 1 2 4 2 0 0 4 3 0 0 0 5 0 3 22 0 0 0 0 0 0 0 0 1 7 2 0 0 0 0 0 0 0 0 3 0 0 0 0 0 0 24 27 61 4 1 0 0 0 1 0 2 0 0 0 0 0 0 0 0 SA2 2007 7 0 0 0 0 2 1 1 28 0 0 3 3 0 3 0 1 0 2 18 0 0 0 0 2 0 2 0 0 5 1 2 0 0 0 0 4 0 1 1 1 4 2 2 2 0 4 37 122 3 0 0 0 0 8 0 2 0 0 1 0 0 0 2 0 SJ2 2007 0 0 0 0 0 0 0 2 1 0 0 0 2 0 2 3 1 0 4 55 0 0 0 1 1 0 2 0 2 0 3 1 0 0 0 0 0 0 7 1 0 0 0 0 0 0 4 23 52 0 0 0 0 0 98 0 0 0 0 0 1 0 0 6 0 SJ3 2007 8 0 3 0 0 8 0 3 1 0 0 1 31 0 0 1 7 0 1 76 0 0 0 2 0 0 5 0 1 2 1 0 0 0 0 1 6 0 1 1 16 2 0 1 0 0 20 35 16 0 0 0 0 0 6 0 0 0 0 0 0 0 0 0 0 SY1 2007 0 0 0 0 1 0 0 0 1 0 0 1 4 0 0 0 0 0 13 43 0 1 0 0 0 0 1 0 13 3 0 0 0 0 0 1 2 0 0 0 0 5 0 0 0 0 7 48 92 9 0 0 0 0 10 0 6 0 0 0 0 0 0 0 0 SY2 2007 0 0 0 0 3 2 0 0 1 0 0 6 2 0 5 0 0 0 4 45 0 0 0 1 1 1 1 0 14 0 0 0 0 0 0 0 3 0 5 1 0 3 0 0 0 0 2 41 83 1 2 0 0 0 12 0 0 0 0 0 1 0 1 0 0 T3 2007 0 0 0 0 3 0 0 0 3 0 0 8 0 0 4 0 0 0 2 51 0 0 0 0 0 0 0 0 0 3 1 1 0 0 0 0 0 0 5 1 0 0 0 0 0 0 4 26 90 31 0 0 0 0 20 0 2 0 0 0 1 0 0 9 0 AB1 2008 0 0 0 0 3 4 0 0 0 0 0 6 0 0 3 0 0 0 1 81 0 0 0 0 0 0 0 0 9 0 3 0 0 0 0 0 0 0 0 0 0 3 1 0 0 0 1 3 4 2 94 0 0 1 1 1 1 0 0 2 0 0 0 0 0 AB3 2008 0 0 0 0 0 0 0 0 0 0 0 7 0 0 2 0 0 0 0 85 2 0 0 0 0 1 0 0 54 0 0 0 0 0 0 1 1 0 0 0 0 0 0 0 1 0 0 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB4 2008 0 0 0 0 0 0 0 0 0 0 0 1 0 0 5 0 0 0 0 138 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 5 0 0 0 0 1 31 45 3 64 0 0 0 3 0 0 0 0 0 0 0 0 0 0 AB5 2008 0 0 0 0 0 0 0 0 0 0 0 3 0 0 3 2 0 0 0 207 0 0 0 0 0 0 0 0 11 4 4 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 6 32 0 0 0 3 11 1 0 0 0 0 0 0 0 0 0 0 AH1 2008 2 0 0 0 0 1 0 1 3 0 0 7 3 0 0 0 10 0 5 54 0 1 0 0 0 0 0 0 5 5 4 0 0 0 0 0 2 0 1 0 1 0 0 0 1 0 9 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT1 2008 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 193 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 1 3 24 1 73 0 0 0 0 2 0 0 0 0 0 0 0 0 0 AT2 2008 0 0 0 0 0 0 0 0 0 0 0 2 0 0 1 1 0 0 48 134 4 2 0 0 0 0 0 0 20 0 3 0 0 1 0 0 5 0 3 0 0 0 0 0 0 0 0 11 4 1 11 0 0 0 4 3 0 0 0 0 0 0 0 0 0 C1 2008 0 0 0 0 0 0 0 0 0 0 0 9 1 0 0 0 0 0 2 244 1 0 0 0 0 0 0 0 4 1 2 0 0 0 0 0 0 0 0 0 0 0 1 0 0 1 1 7 4 3 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C3 2008 5 0 1 0 0 2 0 3 1 0 0 10 5 0 1 0 1 0 2 78 0 3 0 0 0 0 0 0 15 2 2 0 0 0 0 0 0 0 0 0 1 0 0 0 6 0 1 0 2 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 GAV1 2008 0 0 0 0 0 1 0 0 0 0 0 4 2 0 0 2 0 0 3 113 0 0 0 0 0 0 0 0 28 0 7 1 0 0 1 0 0 0 3 0 0 0 0 0 14 0 0 0 0 1 0 0 2 0 1 0 0 0 0 0 0 0 0 0 0 GAV1 2008 0 0 0 0 0 0 0 1 0 0 0 16 3 1 5 0 0 0 3 119 4 0 0 0 0 0 1 0 5 0 7 0 0 0 0 0 0 0 0 0 0 1 3 0 8 0 0 1 2 2 0 0 2 0 1 0 0 0 0 0 0 0 0 0 0 M1 2008 0 0 0 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 273 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 2 0 0 0 0 10 4 0 0 0 0 0 0 0 0 0 M2 2008 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 190 0 0 0 0 0 0 0 0 24 0 2 0 0 0 0 0 0 0 6 0 0 0 0 0 0 0 0 3 0 1 0 1 0 0 3 1 1 0 0 0 0 0 0 0 0 M3 2008 13 0 0 0 3 0 0 12 1 0 1 12 5 0 5 0 13 0 7 72 0 0 0 2 0 0 0 0 8 0 1 0 0 0 0 2 0 0 1 0 0 1 1 0 6 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M4 2008 39 0 0 0 0 2 0 3 1 0 0 0 17 0 0 0 0 0 2 128 0 0 0 0 0 0 0 0 1 0 2 0 0 0 0 0 0 0 0 0 10 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M7 2008 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 220 0 0 0 0 0 0 0 0 37 0 3 0 0 0 0 0 2 0 8 0 0 3 0 0 0 0 0 4 0 0 0 0 0 0 9 0 0 0 0 0 0 0 0 0 0 MONT2 2008 1 0 0 0 1 0 0 0 0 0 0 44 1 0 2 0 0 0 3 78 0 0 0 0 0 0 0 0 35 3 0 0 0 0 0 0 0 0 0 0 0 2 0 4 1 0 4 9 3 4 0 0 2 0 9 0 0 0 0 0 0 0 0 0 0 RIN1 2008 1 0 0 0 0 0 0 0 0 0 0 34 0 0 1 1 4 0 1 110 0 8 0 0 0 0 0 0 44 1 2 0 1 0 0 0 0 0 2 2 1 0 0 1 0 0 1 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SA2 2008 2 0 0 0 0 0 0 0 1 0 0 43 0 0 1 0 0 0 1 61 0 3 0 0 0 0 0 0 0 3 1 0 2 1 0 0 0 0 3 0 4 1 0 2 4 0 0 1 0 1 1 0 1 0 0 0 0 0 0 0 0 0 0 0 0 SJ2 2008 0 0 0 0 0 0 0 1 1 0 1 7 5 0 2 0 1 0 1 98 1 2 0 0 0 0 1 0 18 0 0 0 0 0 0 0 2 0 3 0 0 0 0 0 1 0 2 0 3 9 0 0 0 0 6 0 0 0 0 0 2 0 0 0 0 SY1 2008 0 0 0 0 0 0 0 0 1 0 0 7 0 0 10 0 0 0 0 91 2 0 0 0 0 0 1 0 0 0 0 0 0 0 0 3 1 0 2 0 0 0 1 0 0 0 0 12 11 3 0 0 0 0 1 0 0 0 0 1 0 0 0 0 0 SY2 2008 1 0 0 0 0 0 0 0 0 0 0 20 0 0 35 0 0 0 2 155 0 0 0 1 0 0 0 0 1 0 2 0 0 1 0 1 3 0 3 0 0 5 0 0 0 0 0 14 8 4 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 T3 2008 1 0 0 0 1 1 0 0 1 0 0 17 0 0 2 0 0 0 3 23 0 0 0 0 0 0 0 0 7 0 1 0 0 1 0 0 1 0 0 1 0 1 0 0 2 0 0 5 0 0 1 0 168 0 5 1 0 0 0 1 0 0 1 0 0 AB1 2009 0 0 0 0 5 0 0 0 0 0 0 2 0 0 0 0 0 0 9 69 0 0 0 0 0 0 0 0 43 1 2 0 0 0 0 0 0 0 2 0 0 2 0 0 0 0 5 2 40 8 0 0 0 3 7 0 0 0 0 0 0 0 0 0 0 AB3 2009 0 0 0 0 0 0 0 0 0 0 0 24 0 0 0 0 0 0 4 118 0 0 0 0 0 0 0 0 88 3 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 13 2 2 0 0 0 0 2 0 0 0 0 0 0 1 0 0 0 AB5 2009 0 0 0 0 0 0 0 0 0 0 0 14 0 0 0 0 0 0 1 134 0 0 0 0 16 2 0 0 7 3 3 0 0 0 0 1 1 0 18 0 0 0 0 0 0 0 0 10 10 1 0 0 0 40 0 0 0 0 0 0 0 0 0 0 0 AB6 2009 0 0 0 0 0 0 0 0 0 0 0 0 0 0 17 0 0 0 6 69 1 0 0 0 0 0 0 0 8 3 0 0 0 0 0 0 4 0 3 0 0 4 2 0 0 0 1 42 8 17 34 0 0 0 6 0 0 0 1 0 0 0 0 0 0 AH1 2009 14 0 0 0 0 0 0 1 9 0 0 5 1 0 0 0 24 0 0 50 2 2 0 0 0 0 2 0 0 2 10 1 0 0 0 3 3 0 1 1 2 3 1 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 AT1 2009 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 215 0 0 0 0 0 0 1 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 4 7 0 12 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AT2 2009 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 1 42 7 0 0 0 0 0 0 0 44 0 2 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 3 2 18 81 1 0 0 0 2 0 0 0 0 1 0 0 0 0 0 C1 2009 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 6 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 12 3 0 0 0 1 3 0 0 0 0 0 0 0 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-8 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Va 2 4 4 0 5 2 5 2 3 4 5 5 0 5 9 5 2 0 5 8 8 3 4 6 6 6 5 6 7 3 1 8 8 5 5 3 3 5 5 3 0 5 9 0 3 10 3 7 7 7 9 8 5 9 9 10 4 NA NA NA NA NA NA NA NA S(0-3), M(4-6), TS M M S M S M S S M M M S M T M S S M T T S M M M M M M T S S T T M M S S M M S S M T S S T S T T T T T M T T T M NA NA NA NA NA NA NA NA Primary FFGsh om s sh cf p sc p sh p sh p cg p s p sc sc p NA cg cg p p NA p cg p cf cg NA p p p p NA p p p p p p p p p cg p sc cg cg cg sh cg cg cg pa p cg NA p NA pa NA NA cf Study Reaches Year Lepidostomatidae Leptoceridae Limnophilidae Odontoceridae Philopotamidae Polycentropodidae Psychomyiidae Rhyacophilidae Sericostomatidae Carabidae Dryopidae Dytiscidae Elmidae Gyrinidae Halipidae Hydrophilidae Psphenidae Blephariceridae Ceratopogonidae Chironomidae Culicidae Dixidae Dolichopodidae Empididae Ephydridae Muscidae Psychodidae Sciomyzidae Simulidae Stratiomyidae Tipulidae Belostomatidae Corixidae Gerridae Naucoridae Veliidae Aeshnidae Calypterygidae Coenagrionidae Cordulegastridae Gomphidae Lestidae Libellulidae Corydalidae Sialidae COLLEMBOLA ACARI GASTROPODA OSTRACODA COPEPODA CLADOCERA DECAPODA AMPHIPODA ISOPODA OLIGOCHAETA HIRUDINEA TURBELLARIA Others-no tolerance values Chrysomelidae Hydraenidae Notonectidae LEPIDOPTERA HYMENOPTERA NEMATOMORPHA NEMATODA BIVALIA (CLAM) C3 2009 20 0 0 0 0 2 1 1 7 0 0 8 14 0 0 0 5 0 0 6 0 2 0 0 0 0 0 0 1 5 6 0 0 0 0 0 1 0 0 7 3 1 0 0 0 0 1 5 9 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 GAV1 2009 0 1 0 0 0 0 4 0 1 0 0 5 0 0 5 0 0 0 1 103 1 0 0 2 0 0 0 0 1 0 2 0 1 0 0 0 1 0 2 0 0 0 0 0 2 0 2 0 14 3 0 0 17 0 0 0 0 0 0 0 0 2 0 0 0 M1 2009 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 228 0 0 0 0 0 0 0 0 10 0 4 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 2 3 4 0 0 0 0 2 2 0 0 0 0 2 0 0 0 0 M2 2009 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 124 0 0 0 0 0 0 0 0 53 0 2 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 13 1 1 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 M3 2009 10 0 0 0 5 2 0 7 2 0 0 1 6 0 0 0 5 2 2 95 0 0 0 0 0 0 0 0 14 1 1 1 0 0 0 3 1 0 0 0 0 2 0 0 0 0 5 0 15 6 0 0 0 0 1 0 0 0 0 0 2 0 0 0 0 M4 2009 31 0 0 0 8 0 0 6 2 0 0 1 20 0 1 0 4 0 4 86 0 0 0 1 0 0 5 0 11 1 2 0 0 0 0 2 1 0 11 0 3 0 0 0 0 2 2 2 7 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 M7 2009 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 189 0 0 0 0 0 0 0 0 24 0 2 0 0 0 0 0 1 0 0 0 0 0 0 0 0 1 0 3 0 2 0 0 0 0 7 0 0 0 0 0 0 0 0 0 0 MONT2 2009 4 0 0 0 0 0 0 0 0 0 0 35 4 0 11 0 0 0 1 37 0 1 0 0 0 0 0 0 4 2 2 0 0 0 0 1 2 0 1 0 0 1 0 0 0 0 4 81 60 3 0 0 0 0 20 0 0 0 0 0 2 0 0 0 0 RIN0 2009 0 0 0 0 0 0 1 0 2 0 0 3 0 0 1 0 0 0 0 23 2 0 0 0 0 0 0 0 7 19 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 7 112 1 0 0 0 2 1 0 0 0 0 0 0 0 0 0 0 RIN1 2009 3 0 0 0 0 0 0 0 2 0 0 9 3 0 1 0 6 0 1 108 0 0 0 0 0 0 0 0 5 10 0 1 0 0 0 0 1 0 0 0 0 0 0 0 0 0 1 12 46 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 SA2 2009 2 0 0 0 1 0 2 0 4 0 0 0 3 1 1 0 0 0 0 13 0 0 0 0 0 0 0 0 2 2 2 2 0 0 0 1 9 0 1 0 1 8 0 1 3 0 0 8 205 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 SJ2 2009 0 0 0 0 0 0 0 0 0 0 0 4 3 0 0 0 2 0 1 50 0 0 0 0 0 0 1 0 13 0 0 2 0 0 0 0 0 0 0 0 0 0 0 0 9 0 0 1 0 1 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 SJ3 2009 21 0 2 0 0 4 0 3 2 0 0 3 7 0 0 0 7 0 0 37 0 1 0 0 0 0 0 0 2 4 0 0 0 0 0 1 14 0 9 0 11 4 0 0 0 0 2 8 11 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SY1 2009 0 0 0 0 2 1 0 0 0 0 0 2 0 0 0 0 0 0 4 121 0 0 0 0 5 0 1 0 61 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 15 0 0 0 0 0 4 0 0 0 0 SY2 2009 0 0 0 0 2 0 0 0 1 0 0 4 0 0 0 1 0 0 4 85 0 0 0 0 4 0 0 0 36 5 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 2 0 1 0 0 0 0 0 2 0 0 0 0 0 8 0 0 0 0 T3 2009 0 0 0 0 0 0 0 0 0 0 0 33 0 0 0 0 0 0 3 210 5 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 3 0 0 0 0 12 0 0 0 0 3 0 0 0 0 0 0 0 4 0 0 0 0 0 0 0 0 0 0 AB1 2010 0 0 0 0 11 0 0 0 0 0 0 1 0 0 3 0 0 0 0 90 0 0 0 0 4 0 0 0 80 0 1 0 0 0 0 0 0 0 5 0 0 1 1 0 0 0 1 0 6 0 0 0 0 4 6 1 0 0 0 0 0 0 0 0 0 AB2 2010 0 0 0 0 7 0 0 0 0 0 0 5 0 0 2 0 0 0 0 113 0 0 0 0 6 0 1 0 93 0 1 0 0 1 0 0 0 0 0 0 0 5 0 0 0 0 0 0 0 2 0 0 0 0 0 1 0 0 0 0 0 1 0 0 0 AB3 2010 0 0 0 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 33 0 0 0 0 0 1 0 0 146 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB5 2010 0 0 0 0 0 0 0 0 0 0 0 2 0 0 1 0 0 0 0 206 0 0 0 0 0 0 0 0 36 2 0 0 0 0 0 0 1 0 1 0 0 0 0 0 0 0 0 0 12 3 0 0 4 15 5 0 0 0 0 1 0 0 0 0 0 AB7 2010 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 176 0 0 0 0 0 0 0 0 48 2 2 0 0 0 0 0 0 0 8 0 0 1 1 0 0 1 1 6 20 5 0 0 0 0 4 0 0 0 0 0 0 0 0 0 0 AH1 2010 48 0 0 0 0 1 0 1 6 0 0 2 4 0 0 0 21 0 4 74 0 1 0 0 0 0 0 0 3 0 8 0 0 0 0 1 1 0 1 0 0 0 0 0 1 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 AP1 2010 1 0 0 0 0 1 0 0 0 0 0 16 0 0 10 0 0 0 1 53 0 0 0 2 0 1 1 0 110 0 3 0 0 1 0 0 0 0 1 0 0 0 0 0 0 0 0 41 4 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 AT1 2010 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 1 0 0 0 78 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 8 3 198 0 0 0 7 0 0 0 0 0 0 0 0 0 0 AT2 2010 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 77 0 0 0 1 0 0 0 0 117 1 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 1 1 2 0 0 0 0 26 0 0 0 0 0 0 1 0 0 0 C1 2010 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 136 0 0 0 0 1 0 0 0 5 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 120 7 10 1 0 0 0 13 0 5 0 0 0 0 0 0 0 0 C3 2010 12 0 2 0 0 4 0 5 2 0 0 14 3 0 0 0 2 0 1 54 0 0 0 0 0 0 1 0 14 0 0 0 0 0 0 1 0 0 1 1 0 0 0 0 7 0 0 1 5 0 0 0 0 0 6 0 0 0 0 0 0 0 0 0 2 GAV1 2010 0 0 0 0 0 0 0 0 1 0 0 3 0 0 0 0 0 0 1 96 0 0 0 1 0 0 0 0 1 0 1 0 1 0 1 0 0 0 3 0 0 0 0 0 19 0 0 0 0 7 4 0 0 0 2 0 0 0 0 0 0 0 0 0 1 M1 2010 0 0 0 0 0 0 0 0 0 0 0 0 1 0 3 0 0 0 0 189 0 0 0 0 3 0 2 0 55 1 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 1 0 1 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 M2 2010 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 138 0 0 0 1 0 0 0 0 85 0 1 0 0 0 0 0 0 0 5 0 0 0 0 0 0 0 0 3 1 3 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 M3 2010 0 0 0 0 1 0 0 1 0 0 0 0 4 0 0 0 3 0 0 129 0 0 0 0 0 0 1 0 48 0 0 0 0 0 0 1 0 0 0 0 0 3 0 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 M4 2010 0 0 0 0 0 0 0 0 0 0 0 4 2 0 1 0 0 4 0 164 0 0 0 2 0 0 3 0 32 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 MONT2 2010 0 0 0 0 0 0 0 0 0 0 0 4 2 0 1 0 1 0 0 125 10 0 0 0 0 0 0 0 35 2 1 1 0 0 0 0 0 0 0 0 0 0 0 0 4 0 2 0 1 2 0 0 0 0 9 0 0 0 0 0 0 0 0 0 1 RIN0 2010 0 0 0 0 0 0 1 0 0 0 0 8 0 0 1 0 0 0 0 49 0 0 0 0 0 0 0 0 58 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 1 0 0 1 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 RIN1 2010 6 0 0 0 0 2 2 0 16 0 0 6 0 1 1 0 1 0 2 91 0 2 0 0 1 0 0 0 1 0 0 3 0 0 0 0 0 0 1 1 1 0 0 0 0 0 0 4 2 1 0 0 0 0 1 0 0 0 0 1 0 0 0 0 0 SA2 2010 0 0 0 0 3 0 0 0 0 0 2 5 0 0 2 0 0 0 4 98 0 0 0 0 0 1 0 0 12 1 1 2 0 0 0 3 0 0 0 1 1 0 0 0 0 0 1 1 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 SJ2 2010 8 0 0 0 0 0 0 0 0 0 0 6 1 0 3 0 0 0 66 129 0 0 0 2 1 2 0 0 29 0 1 1 0 0 0 0 0 0 2 0 1 0 0 0 0 0 0 1 0 3 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 SJ3 2010 18 0 1 0 0 1 0 2 0 0 2 2 13 0 0 0 4 0 0 104 0 1 0 0 0 0 0 0 1 0 2 0 0 0 0 2 2 0 2 1 12 1 0 0 3 0 4 6 0 0 0 0 0 1 11 0 0 0 0 0 0 0 0 0 0 SY1 2010 0 0 0 0 0 0 0 0 0 0 0 3 0 0 2 0 0 0 0 108 0 0 0 0 0 0 2 0 41 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 4 0 0 0 0 4 0 0 0 0 0 0 0 0 0 0 SY2 2010 0 0 0 0 1 0 0 0 2 0 0 4 0 0 2 0 0 0 1 96 0 0 0 0 0 0 0 0 60 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 T3 2010 0 0 0 0 0 0 0 0 0 0 0 5 0 0 0 0 0 0 0 61 0 0 0 1 0 0 0 0 4 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 13 0 0 0 0 0 0 0 0 0 0 AB1 2011 0 0 0 0 0 0 0 0 0 0 0 8 0 0 4 0 0 0 1 65 0 0 0 0 0 0 0 0 1 0 1 0 0 0 0 0 0 0 2 1 0 0 0 0 0 0 0 0 4 3 0 0 0 110 17 0 0 0 0 0 1 0 0 0 0 AB3 2011 2 0 0 0 7 0 0 0 1 0 0 6 1 0 1 1 0 0 1 82 0 0 0 0 0 0 0 0 29 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 AB5 2011 0 0 0 0 0 0 0 0 0 0 0 29 0 0 0 0 0 0 0 171 0 0 0 2 1 2 1 0 16 0 4 0 0 1 0 0 1 0 0 0 0 0 0 0 0 0 1 7 10 4 0 0 1 46 2 0 0 0 0 0 0 0 0 0 0 AB7 2011 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 84 0 0 0 3 0 0 0 0 4 3 1 0 0 0 0 0 0 0 14 0 0 0 0 0 0 0 0 9 3 4 0 0 2 0 4 13 0 0 0 1 0 0 0 0 0 AH1 2011 3 0 0 0 2 0 0 1 11 0 0 2 0 0 0 0 3 0 5 41 0 1 0 0 0 0 0 0 13 2 6 0 0 0 0 1 0 0 1 0 1 1 0 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 C1 2011 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 173 0 2 0 0 0 0 0 0 34 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 1 0 0 3 0 0 0 0 17 0 0 0 0 0 0 0 0 0 0 C3 2011 5 0 0 0 1 0 2 4 0 0 0 5 3 0 0 0 1 0 2 10 0 3 0 0 0 0 0 0 0 5 0 0 0 1 0 1 0 0 0 0 0 0 0 0 1 0 1 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 1 0 0 EC1 2011 5 0 0 0 1 1 0 1 2 0 0 9 0 0 1 0 0 0 0 104 0 0 0 0 0 0 0 0 0 1 1 0 2 0 0 0 0 0 0 0 0 1 0 0 1 0 0 1 0 1 0 0 0 3 7 0 0 0 0 0 0 0 0 0 0 GAV1 2011 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 0 0 5 161 0 0 0 0 1 1 0 0 3 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 4 0 1 0 1 0 0 0 2 0 0 0 0 0 0 0 0 0 0 0 0 M1 2011 0 0 0 0 0 0 0 0 0 0 0 1 0 1 0 0 0 0 1 156 0 0 0 0 1 0 1 0 26 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 8 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 M2 2011 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 1 0 0 0 111 0 0 0 0 0 0 0 0 46 0 8 0 0 0 0 0 0 0 5 0 0 0 0 0 0 0 0 5 0 0 0 0 0 0 4 0 0 0 0 0 0 0 0 0 0 M3 2011 10 0 0 0 3 0 0 2 0 0 0 5 6 0 0 0 2 1 1 93 0 0 0 0 0 0 1 0 22 0 0 0 0 0 0 0 0 0 1 1 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 M4 2011 18 0 0 0 3 0 0 6 0 0 0 1 4 0 0 0 0 2 1 97 0 0 0 0 0 0 0 0 2 0 2 0 0 0 0 0 0 0 0 0 0 1 0 1 0 0 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SJ2 2011 6 0 0 0 0 0 0 1 0 0 0 7 4 0 0 0 0 0 4 187 0 0 0 0 0 0 1 0 25 0 0 1 0 0 0 1 0 0 1 0 0 0 0 0 1 0 0 0 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SY1 2011 0 0 0 0 24 0 0 0 1 0 0 24 0 0 1 0 0 0 1 104 0 0 0 1 0 0 6 0 8 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 2 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 SY2 2011 0 0 0 0 2 0 0 0 0 0 0 18 0 0 1 0 0 0 2 60 0 0 0 0 0 0 0 0 3 0 2 0 0 1 0 0 0 0 0 0 0 2 0 0 0 0 0 2 0 0 0 0 0 1 2 0 0 0 0 0 0 0 0 0 0 AB1 2012 0 0 0 0 7 0 0 0 0 0 0 0 0 0 0 0 0 0 0 30 0 0 0 1 0 0 0 0 4 4 0 0 0 0 0 0 1 0 0 0 0 1 0 0 0 0 2 0 0 5 0 0 0 179 2 0 0 0 0 0 0 0 1 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-9 Ecology Consultants, Inc. Table A-1: Streams Physiochemical and BMI Data, 2000-2014

Tolerance Va 2 4 4 0 5 2 5 2 3 4 5 5 0 5 9 5 2 0 5 8 8 3 4 6 6 6 5 6 7 3 1 8 8 5 5 3 3 5 5 3 0 5 9 0 3 10 3 7 7 7 9 8 5 9 9 10 4 NA NA NA NA NA NA NA NA S(0-3), M(4-6), TS M M S M S M S S M M M S M T M S S M T T S M M M M M M T S S T T M M S S M M S S M T S S T S T T T T T M T T T M NA NA NA NA NA NA NA NA Primary FFGsh om s sh cf p sc p sh p sh p cg p s p sc sc p NA cg cg p p NA p cg p cf cg NA p p p p NA p p p p p p p p p cg p sc cg cg cg sh cg cg cg pa p cg NA p NA pa NA NA cf Study Reaches Year Lepidostomatidae Leptoceridae Limnophilidae Odontoceridae Philopotamidae Polycentropodidae Psychomyiidae Rhyacophilidae Sericostomatidae Carabidae Dryopidae Dytiscidae Elmidae Gyrinidae Halipidae Hydrophilidae Psphenidae Blephariceridae Ceratopogonidae Chironomidae Culicidae Dixidae Dolichopodidae Empididae Ephydridae Muscidae Psychodidae Sciomyzidae Simulidae Stratiomyidae Tipulidae Belostomatidae Corixidae Gerridae Naucoridae Veliidae Aeshnidae Calypterygidae Coenagrionidae Cordulegastridae Gomphidae Lestidae Libellulidae Corydalidae Sialidae COLLEMBOLA ACARI GASTROPODA OSTRACODA COPEPODA CLADOCERA DECAPODA AMPHIPODA ISOPODA OLIGOCHAETA HIRUDINEA TURBELLARIA Others-no tolerance values Chrysomelidae Hydraenidae Notonectidae LEPIDOPTERA HYMENOPTERA NEMATOMORPHA NEMATODA BIVALIA (CLAM) AB3 2012 2 0 0 0 0 1 0 0 1 0 0 6 2 0 1 0 0 0 1 22 0 0 0 0 0 0 2 0 4 93 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 32 60 0 0 0 1 1 2 0 1 0 0 0 1 0 0 0 0 AB5 2012 0 0 0 0 5 0 0 0 0 0 0 8 0 0 3 0 0 0 0 82 0 0 0 2 1 0 0 0 6 0 1 0 0 0 0 2 0 0 9 0 0 0 0 0 0 7 0 7 3 0 0 0 74 57 19 0 3 0 0 0 0 0 0 0 0 AH1 2012 52 0 1 0 0 1 0 6 13 0 0 0 4 0 0 0 5 0 4 63 0 0 0 0 0 0 1 0 0 2 5 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 2 2 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 1 C1 2012 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 33 0 0 0 0 0 1 0 0 1 1 1 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 46 11 4 106 0 0 0 89 0 0 0 0 0 0 0 0 0 4 C3 2012 28 0 0 0 0 0 0 2 8 0 0 3 11 0 0 0 0 0 1 102 0 0 0 0 0 0 0 0 0 8 1 0 0 1 0 0 0 0 1 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 1 0 4 GAV1 2012 4 0 0 0 0 0 1 0 4 0 0 2 1 0 0 0 0 0 1 6 0 0 0 0 0 0 0 0 0 1 1 0 0 0 0 0 0 0 2 1 0 0 0 0 0 0 1 1 8 0 0 0 11 0 0 0 0 0 0 0 0 0 0 0 1 M1 2012 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 1 87 0 0 0 0 0 1 1 0 5 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 1 0 1 0 0 0 0 16 0 0 0 0 0 0 1 0 0 0 M3 2012 12 0 0 0 2 0 0 6 6 0 1 2 12 0 0 0 8 1 4 40 0 0 0 0 0 0 0 0 20 5 0 0 0 1 0 1 0 0 1 0 0 2 0 0 0 0 7 3 5 12 0 0 0 0 6 0 2 0 0 0 0 0 0 0 0 M4 2012 49 0 0 0 0 0 0 12 0 0 0 2 8 0 0 0 2 0 0 96 0 0 0 0 0 0 1 0 0 0 0 0 0 2 0 0 2 0 0 1 0 0 0 0 0 0 0 5 13 0 0 0 0 0 2 0 3 0 0 0 0 0 1 0 0 R0 2012 3 0 0 0 9 1 2 6 11 0 0 2 1 0 0 0 2 0 3 76 0 2 0 1 0 0 4 0 12 0 3 0 0 0 0 1 0 0 1 0 0 0 0 0 0 0 2 5 1 0 0 0 0 1 1 0 0 0 0 1 0 0 0 0 0 SJ2 2012 1 0 0 0 0 0 0 1 5 0 0 2 16 0 0 0 0 0 2 23 0 0 0 0 0 0 1 0 1 2 0 0 0 0 0 0 0 0 0 0 2 0 0 0 3 0 2 20 7 2 0 0 0 0 8 0 2 0 0 0 0 0 0 0 0 SY1 2012 0 0 0 0 15 0 2 0 1 0 0 1 4 0 2 0 0 0 6 101 0 0 0 0 0 0 0 0 15 0 1 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 7 25 2 5 0 0 0 0 18 0 6 0 0 0 0 0 0 0 0 SY2 2012 0 0 0 0 7 0 1 0 3 0 0 4 1 0 1 0 1 0 5 106 0 0 0 1 0 0 0 0 26 2 0 1 0 0 0 0 0 0 4 0 0 0 0 0 0 0 1 3 3 1 0 0 0 0 13 0 2 0 0 0 0 0 0 0 0 AB1 2013 0 0 0 0 25 0 0 0 3 0 0 7 0 0 1 0 0 0 2 95 0 0 0 0 0 0 0 0 35 0 1 0 0 0 0 0 2 0 3 0 0 0 0 0 0 0 0 1 1 0 0 0 1 94 1 0 2 0 0 0 1 0 0 0 0 AB3 2013 0 0 0 0 0 0 0 0 1 0 0 8 1 0 0 0 0 0 0 146 0 1 0 0 0 0 1 0 0 0 2 0 0 1 0 0 0 0 0 0 0 4 0 0 0 0 0 24 84 0 3 0 0 0 14 0 4 0 0 0 0 0 0 0 0 AB5 2013 0 0 0 0 2 0 0 0 0 0 0 7 0 0 4 1 0 0 1 94 0 0 0 2 0 0 1 0 9 0 1 0 0 0 0 0 0 0 4 0 0 0 0 0 0 0 0 39 12 12 0 0 2 29 5 0 0 0 0 0 0 0 0 0 0 AH1 2013 17 0 0 0 5 7 0 7 0 0 0 1 3 0 0 0 15 0 4 81 0 5 0 0 0 0 9 0 1 1 8 0 0 0 0 14 1 0 1 1 0 0 0 0 2 0 2 5 0 1 0 0 0 2 0 0 0 1 0 0 0 0 0 0 1 C1 2013 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 35 0 0 0 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 25 4 0 13 0 0 0 75 0 1 0 0 0 0 0 0 0 6 C3 2013 33 0 0 0 0 0 0 3 1 0 0 4 5 0 0 0 0 0 3 135 1 0 0 1 0 0 1 0 18 0 0 1 0 0 0 2 2 0 1 0 0 1 0 0 0 0 0 4 0 0 0 0 0 1 0 0 1 0 0 0 0 0 0 0 3 GAV1 2013 14 0 0 0 0 2 0 0 3 0 0 0 0 0 0 0 0 0 5 72 0 1 0 0 0 0 0 0 0 0 0 0 6 0 0 0 0 0 5 0 0 1 0 0 10 0 0 0 19 3 0 0 10 0 2 0 6 0 0 0 0 0 0 0 5 M1 2013 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 0 240 0 0 0 0 0 0 0 0 19 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 13 0 2 0 13 0 12 0 0 0 0 0 0 0 0 M2 2013 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 103 0 0 0 0 0 0 0 0 0 0 12 0 0 0 0 0 0 0 20 0 0 0 0 0 0 0 0 140 2 4 0 1 0 0 9 0 0 0 0 0 1 0 0 0 0 M3 2013 0 0 0 0 0 0 0 7 0 0 0 1 17 0 0 0 1 0 9 79 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 0 1 0 0 2 0 0 0 0 0 7 106 0 0 0 0 0 16 0 12 0 0 0 0 0 0 0 1 M4 2013 7 0 0 0 0 5 1 1 0 0 0 0 7 0 1 0 1 0 6 142 0 0 0 1 0 0 1 0 4 0 2 0 0 1 0 0 2 0 1 0 0 7 0 0 0 0 0 4 20 0 0 0 0 0 0 0 1 0 0 4 0 0 0 0 0 SA2 2013 0 0 0 0 0 0 0 0 2 0 0 5 0 0 0 0 2 0 1 57 1 5 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 16 0 0 1 0 0 38 18 1 0 0 0 0 3 0 0 0 0 0 1 0 0 0 0 SJ2 2013 0 0 0 0 0 1 0 0 34 0 0 0 7 0 0 0 0 0 4 52 0 1 0 0 0 0 1 0 0 0 2 1 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 3 29 0 0 0 0 0 11 0 0 0 0 0 0 0 0 0 0 SY1 2013 0 0 0 0 0 0 1 0 3 0 0 5 2 0 4 0 0 0 0 18 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 4 186 22 24 0 0 0 0 1 0 12 0 0 0 0 0 0 0 0 SY2 2013 0 0 0 0 0 0 0 1 13 0 0 0 5 0 2 0 0 0 4 152 0 1 0 0 0 0 0 0 7 1 3 0 0 1 0 0 0 0 14 0 0 3 0 0 3 0 0 18 11 1 0 0 0 0 12 0 5 0 0 0 0 0 0 0 0 AB1 2014 0 0 0 0 0 0 0 0 0 0 0 1 0 0 1 0 0 0 0 142 0 0 0 0 0 0 0 0 10 0 1 0 0 0 0 0 0 0 1 0 0 0 0 0 1 0 1 10 1 2 0 0 0 27 4 0 1 0 0 0 0 0 1 0 3 AB3 2014 0 0 0 0 0 0 0 0 0 0 0 7 0 0 0 1 0 0 2 67 1 0 0 0 0 0 0 0 75 0 1 0 0 1 0 0 0 0 0 0 0 0 0 1 0 0 3 3 9 0 1 0 0 0 4 0 0 0 0 0 0 0 0 0 0 AB5 2014 0 0 0 0 0 0 0 0 0 0 0 8 0 0 0 0 0 0 0 80 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 30 65 24 3 0 34 2 4 0 1 0 0 0 0 0 0 0 0 AH1 2014 4 0 0 0 28 0 0 3 3 0 0 3 4 0 0 0 5 0 2 135 0 2 0 2 0 0 0 0 22 0 0 0 0 0 0 0 0 0 5 0 0 0 0 0 0 0 1 2 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 C1 2014 0 0 0 0 0 0 0 0 0 0 0 0 0 0 3 0 0 0 0 40 1 0 0 0 0 1 0 0 2 0 0 0 0 0 0 0 0 0 5 0 0 0 0 0 0 0 4 51 108 5 7 0 0 0 9 0 1 0 0 0 0 0 0 0 4 C3 2014 0 0 0 0 2 0 0 0 0 0 0 5 2 0 0 0 0 1 0 93 0 0 0 1 0 0 0 0 122 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 1 5 0 0 0 0 0 0 0 0 0 2 GAV1 2014 0 0 0 0 0 0 0 0 0 0 0 10 0 0 0 0 1 0 0 134 2 0 0 1 0 0 1 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 5 12 2 7 0 0 14 0 1 0 0 0 0 0 0 0 0 0 0 M1 2014 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 102 0 0 0 1 0 0 0 0 7 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 5 11 0 0 2 0 22 0 8 0 0 0 0 0 0 0 1 M2 2014 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 232 0 0 0 4 0 0 0 0 11 0 0 0 0 0 0 0 0 0 15 0 0 0 0 0 0 0 0 27 2 3 0 1 0 0 5 0 0 0 0 0 0 0 0 0 0 M3 2014 3 0 0 0 1 0 0 1 4 0 0 6 5 0 0 0 2 0 0 131 0 0 0 3 0 0 1 0 28 1 0 1 0 0 0 0 0 0 2 0 0 8 0 0 0 0 1 7 32 16 0 0 0 0 4 3 0 0 0 1 0 0 0 0 10 M4 2014 0 0 0 0 1 0 0 0 1 0 0 4 4 0 1 0 1 0 3 71 0 0 0 2 0 0 0 0 61 0 1 2 0 0 0 0 1 0 6 0 0 3 0 0 0 1 2 6 70 4 0 0 0 0 6 0 4 0 0 0 0 1 0 0 0 SJ2 2014 0 0 0 0 8 0 0 1 2 0 0 0 1 0 0 0 0 0 4 140 26 0 0 1 0 0 1 0 50 2 1 1 0 0 0 0 0 0 7 0 0 0 0 0 0 0 1 1 1 1 0 0 0 0 5 0 0 0 0 0 2 0 0 0 0 SY2 2014 0 0 0 0 1 0 0 2 2 0 0 0 3 0 0 0 1 0 8 135 0 0 0 2 0 0 0 0 42 0 0 0 0 0 0 0 1 0 22 0 0 0 0 0 0 0 1 8 15 5 0 0 0 0 3 0 1 0 0 0 0 0 0 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Appendix A Page A1-10 Ecology Consultants, Inc. Table A-2 Plant Species Observed at Stream Study Reaches, 2014

Family Common Name Scientific Name Study Reaches C1 C3 SY2 M1 M2 M3 M4 AB1 AB3 AB5 SJ2 AH1 GAV1 Native Trees Aceraceae Big-leaf maple Acer macrophyllum 1 1 Aceraceae Box elder Acer negundo 1 1 1 Betulaceae White alder Alnus rhombifolia 1 1 1 1 1 1 1 1 1 Fagaceae Coast live oak Quercus agrifolia 1 1 1 1 1 1 1 1 1 1 1 Jugulandaceae Southern black walnut Juglans californica 1 1 1 1 1 1 1 Lauraceae California bay Umbellularia californica 1 1 1 1 1 Platanaceae Sycamore Platanus racemosa 1 1 1 1 1 1 1 1 1 1 1 1 1 Salicaceae Black cottonwood Populus balsamifera trichocarpa 1 1 1 1 1 1 1 1 1 Salicaceae Fremont cottonwood Populus fremontii fremontii 1 Salicaceae Arroyo willow Salix lasiolepis 1 1 1 1 1 1 1 1 1 1 1 1 1 Salicaceae Red willow Salix laevigata 1 1 1 1 1 1 1 1 1 1 1 1 Native Shrubs, Vines, and Herbs Anacardiaceae Laurel sumac Malosma laurina 1 1 1 Anacardiaceae Lemonade berry Rhus integrifolia 1 1 1 1 1 1 Anacardiaceae Poison oak Toxicodendron diversilobum 1 1 1 1 1 1 1 1 1 1 1 Asteraceae California sagebrush Artemesia californica 1 1 1 1 1 1 1 1 1 Asteraceae Mugwort Artemesia douglasiana 1 1 1 1 1 1 1 1 1 1 1 1 1 Asteraceae Coyote brush Baccharis pilularis 1 1 1 1 1 1 1 1 1 1 1 Asteraceae Plummer's baccharis Baccharis plummerae plummerae 1 1 1 Asteraceae Mulefat Baccharis salicifolia 1 1 1 1 1 1 1 1 1 Asteraceae California bush sunflower Encelia californica 1 1 Asteraceae Prickly ox tongue Picris echioides 1 1 1 1 1 1 1 1 1 1 Asteraceae Goldenrod Solidager californica 1 Asteraceae Canyon sunflower Venegasia carpesioides 1 1 1 1 1 1 1 1 1 Asteraceae Cocklebur Xanthium spinosum 1 1 1 1 1 1 1 1 Brassicaceae Watercress Rorippa nasturtium-aquaticum 1 1 1 1 1 1 1 1 1 1 Caprifoliaceae California honeysuckle Lonicera hispidula var. vacillans 1 1 1 1 Caprifoliaceae Mexican elderberry Sambucus mexicana 1 1 1 1 1 1 1 1 1 1 1 1 1 Caprifoliaceae Creeping snowberry Symphoricarpos mollis 1 1 1 1 1 1 Convolvulaceae Morning glory Calystegia macrostegia cyclostegia 1 1 Cornaceae Dogwood Cornus sp. 1 1 1 1 Crassulaceae Live-forever Dudleya sp. 1 Cucurbitaceae Wild cucumber Marah macrocarpus 1 1 1 Cyperaceae Sedge Carex sp. 1 1 1 1 1 Cyperaceae Cyperus Cyperus spp. 1 1 1 1 1 1 1 1 1 1 Cyperaceae Bulrushes Scirpus spp. 1 1 1 1 Datiscaceae Durango root Datisca glomerata 1 1 1 1 Dennstaedtiaceae Giant chain fern Woodwardia fimbriata 1 1 1 1 1 Dryopteridaceae Wood fern Dryopteris arguta 1 1 1 1 1 Equisetaceae Horsetail Equisetum spp. 1 1 1 1 1 1 1 1 1 1 1 Fabacae Wild sweet pea Lathyrus vestitus var. vestitus 1 1 1 1 1 1 1 1 1 1 1 Fabacae Deerweed Lotus scoparius 1 1 Fagaceae Scrub oak Quercus berberdifolia 1 1 1 Grossulariaceae Chapparal currant Ribes malvaceum 1 Grossulariaceae Fuscia-flowered gooseberry Ribes speciosum 1 1 1 1 1 1 1 Grossulariaceae Gooseberry Ribes sp. 1 1 Hydrophyllaceae Yerba santa Eriodictylon crassifolium Hydrophyllaceae Branching phacelia Phacelia ramosissima 1 1 Hydrophyllaceae Fiesta flower Pholistoma auritum var. auritum 1

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A2-11 Ecology Consultants, Inc. Table A-2 Plant Species Observed at Stream Study Reaches, 2014

Family Common Name Scientific Name Study Reaches C1 C3 SY2 M1 M2 M3 M4 AB1 AB3 AB5 SJ2 AH1 GAV1 Juncaceae Rushes Juncus spp. 1 1 1 1 1 1 Lamiaceae Purple sage Salvia leucophylla 1 1 Lamiaceae Black sage Salvia mellifera 1 1 1 1 Lamiaceae Crimson pitcher sage Salvia spathacea 1 1 Lamiaceae Wood mint, hedge nettle Stachys bullata 1 1 1 1 1 Liliaceae Humboldt lily Lilium humboldtii humboldtii 1 1 Onagraceae Willow herb Epilobium ciliatum 1 1 1 1 1 1 Onagraceae California fuschia Epilobium canum ssp. canum Onagraceae Hooker's evening primrose Oenothera elata ssp. hirsutissma Orchidaceae Stream orchid Epipactis gigantea 1 Oxalidaceae Oxalis Oxalis albicans Papaveraceae California poppy Eschscholzia californica 1 Papaveraceae Bush poppy Dendromecon rigida Poaceae Giant ryegrass Elymus condensatus 1 1 1 1 1 1 1 1 Polygonaceae Ashyleaf buckwheat Eriogonum cinereum 1 Polygonaceae California buckwheat Eriogonum fasciculatum 1 Polygonaceae Water smartweed Polygonum amphibium var. emersum 1 1 1 1 1 1 1 1 Polypodiaceae California polypody Polypodium californicum 1 Potamogetonaceae Pondweeds Potamogeton spp. 1 1 1 1 1 1 1 1 Pteridaceae Venus-hair fern Adiantum capillus-verneris 1 1 1 Ranunculaceae Virgin's bower Clematis ligustifolia 1 1 1 1 1 1 1 1 1 Ranunculaceae Meadow rue Thalictrum fendlerli var. polycarpum 1 1 1 1 Rhamnaceae Buck brush Ceanothus cuneatus 1 1 1 1 Rhamnaceae Hairy-leaved ceanothus Ceanothus oliganthus Rhamnaceae Big pod ceanothus Ceanothus megacarpus Rhamnaceae Greenbark ceanothus Ceanothus spinosus 1 1 Rhamnaceae Coffee berry Rhamnus californica 1 1 1 1 Rhamnaceae Redberry Rhamnus crocea 1 1 Rhamnaceae Hollyleaf redberry Rhamnus ilicifolia Rosaceae Mountain mahogany Cercocarpus betuloides 1 1 1 Rosaceae Toyon Heteromeles arbutifolia 1 1 1 1 1 1 1 1 Rosaceae Holly-leaf cherry Prunus ilicifolia 1 Rosaceae California rose Rosa californica 1 1 1 1 Rosaceae California blackberry Rubus ursinus 1 1 1 1 1 1 1 1 1 1 1 1 Salicaceae Narrow-leaved willow Salix exigua 1 1 Saururaceae Yerba mansa Anemopsis californica 1 Scrophulariaceae Annual paintbrush Castilleja minor ssp. spiralis Scrophulariaceae Heart-leaved penstemon Keckiella cordifolia 1 1 1 1 Scrophulariaceae Bush monkey flower Mimulus aurantiacus 1 1 1 1 1 Scrophulariaceae Scarlet monkey flower Mimulus cardinalis 1 1 1 1 1 1 Scrophulariaceae California figwort Scrophularia californica 1 1 1 1 1 1 1 1 1 1 Solanaceae White nightshade Solanum douglasi 1 1 1 1 1 1 1 1 1 Solanaceae Purple nightshade Solanum xanti 1 1 1 1 Typhaceae Cattails Typha spp. 1 1 1 1 1 1 1 Urticaceae Stinging nettle Urtica dioica 1 1 1 Verbenaceae Western vervain Verbena lasiostachys 1 Vitaceae Wild grape Vitis gidiana Non-Native Trees 1 Anacardiaceae Peruvian pepper tree Schinus molle Myoporaceae Myoporum Myoporum laetum 1 1 Myrtaceae Eucalyptus Eucalyptus spp. 1 1 1 1 1

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A2-12 Ecology Consultants, Inc. Table A-2 Plant Species Observed at Stream Study Reaches, 2014

Family Common Name Scientific Name Study Reaches C1 C3 SY2 M1 M2 M3 M4 AB1 AB3 AB5 SJ2 AH1 GAV1 Pittosporaceae Pittosporum Pittosporum sp. 1 1 1 Tamaricaceae Tamarisk Tamarisk spp. Non-Native Shrubs, Vines, and Herbs Apiaceae Poison hemlock Conium maculatum 1 1 1 1 1 1 1 1 1 Apiaceae Sweet fennel Foeniculum vulgare 1 1 1 1 1 1 1 1 1 Apocynaceae Periwinkle Vinca major 1 1 1 1 1 1 1 1 Araliaceae English ivy Hedera helix 1 1 1 1 1 1 Asteraceae Thoroughwort Ageratina ademorpha 1 1 1 Asteraceae Italian thistle Cardus pycnocephalus 1 1 Asteraceae Brassbuttons Cortula coronopifolia 1 Asteraceae Cudweed Gnaphalium luteo-album 1 1 1 1 Asteraceae Cape ivy (formerly German ivy) Senecio mikanioides 1 1 1 1 1 1 1 Asteraceae Common sow thistle Sonchus oleraceus 1 1 1 Asteraceae Milk thistle Silybum marianum 1 1 1 1 Brassicaceae Black mustard Brassica nigra 1 1 1 1 1 1 1 1 1 1 Brassicaceae Wild radish Raphanus sativus 1 1 1 1 1 1 Caprifoliaceae Japanese honeysuckle Lonicera japonica 1 Cyperaceae Cyperus Cyperus spp. 1 1 1 Euphorbiaceae Castor bean Ricinus communis 1 1 1 1 1 Fabaceae Broom Cytisus sp. 1 Fabaceae Bur-clover Medicago polymorpha ssp. hispida 1 1 1 1 1 1 Fabaceae Sweetclover Melilotus alba 1 1 1 1 Geraniaceae White-stem filaree Erodium moschatum 1 Lamiaceae Horehound Marubium vulgare 1 Lamiaceae Spearmint Mentha spicata var. spicata 1 1 1 1 1 1 Oxalidaceae Bermuda buttercup Oxalis pes-caprae 1 1 1 Plantaginaceae Common plantain Plantago major 1 1 1 1 1 1 1 Poaceae Bent grass Agrostis viridis 1 1 1 Poaceae Giant reed Arundo donax 1 1 1 Poaceae Wild oats Avena fatua 1 1 Poaceae Rescue grass Bromus catharticus 1 1 1 1 Poaceae Ripgut brome Bromus diandrus 1 1 1 1 Poaceae Pampas grass Cortaderia selloana 1 Poaceae Bermuda grass Cynodon dactylon 1 1 1 1 1 1 Poaceae Harding grass Phalaris aquatica 1 1 1 1 Poaceae Smilo grass Pipatherum milaceum 1 1 1 1 1 1 1 1 1 Poaceae Rabbitfoot grass, beard grass Polypogon monspeliensis 1 1 1 1 1 1 1 1 Polygonaceae Curly dock Rumex crispus 1 1 1 1 1 1 Primulaceae Scarlet pimpernel Anagallis arvensis 1 1 1 1 1 1 Rosaceae Himalayan blackberry Rubus discolor 1 1 1 1 1 Scrophulariaceae Water speedwell Veronica anagallis-aquatica 1 1 1 1 1 1 Solanaceae Tree tobacco Nicotiana glauca 1 1 1 1 1 1 1 1 Tropaeolaceae Garden nasturtium Tropaeolum majus 1 1 1 1 native plant species 35 57 19 20 37 43 37 30 37 34 33 39 39 -native plant species 21 12 22 23 15 17 1 26 6 9 16 11 21 Total # plant species 56 69 41 43 52 60 38 56 43 43 49 50 60 % native species 62.5 82.6 46.3 46.5 71.2 71.7 97.4 53.6 86.0 79.1 67.3 78.0 65.0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A2-13 Ecology Consultants, Inc. Table A-3 Vertebrate Species Observed at Streams Study Reaches, 2014

Study Reaches Family Common Name Scientific Name C1 C3 SY3 M1 M2 M3 M4 AB1 AB3 AB5 C1 C3 SJ2 AH1 GAV1 CYPRINIDAE Arroyo chub (introduced) Gila orcutti 1 1 GASTEROSTEIDAE Three-spine stickle back Gasterosteus acleatus 1 1 1 1 1 POECILIIDAE Mosquito fish (introduced) Gambusia affinis 1 1 1 SALMONIDAE Steelhead/rainbow trout Oncorhynchus mykiss 1 1 1 1 1 1 BUFONIDAE Western toad Bufo boreas 1 1 1 HYLIDAE California tree frog Pseudacris cadaverina 1 1 1 1 HYLIDAE Pacific tree frog Pseudacris regilla 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 SALMANDRIDAE California newt Taricha torosa 1 1 1 1 1 ANGUIDAE Alligator lizard Elgaria multicarinata 1 1 1 COLUBRIDAE Gopher snake Pituophis melanoleucus 1 COLUBRIDAE California mountain kingsnake Lampropeltus zonata 1 COLUBRIDAE Two-striped garter snake ThamnophIs hammondii 1 1 EMYDIDAE Western pond turtle Clemmys marmorata 1 1 1 PHRYNOSOMATIDAE Western fence lizard Sceloporus occidentalis 1 1 1 1 1 1 1 1 1 PHRYNOSOMATIDAE Side-blotched lizard Uta stansburiana 1 1 VIPERIDAE Western rattlesnake Crotalus viridis ACCIPITRIDAE Cooper's hawk Accipiter cooperi 1 1 1 ACCIPITRIDAE Red-shouldered hawk Buteo lineatus 1 1 1 1 1 1 1 1 1 ACCIPITRIDAE Red-tailed hawk Buteo jamaicensis 1 1 1 1 1 1 1 1 AEGITHALIDAE Bushtit Psaltriparus minimus 1 1 1 1 1 1 1 1 1 1 1 ALCEDINIDAE Belted kingfisher Ceryle aclyon 1 ANATIDAE Mallard Anas platyrhynchos 1 1 1 1 1 1 1 1 1 1 1 ANATIDAE Cinnamon teal Anas cyanoptera ANATIDAE American widgeon Anas americana APODIDAE Vaux's swift Chaetura vauxi 1 ARDEIDAE Snowy egret Egretta thula 1 ARDEIDAE Great blue heron Ardea heriodas 1 1 ARDEIDAE Green-backed heron Butorides striatus 1 BOMBYCILLIDAE Cedar waxwing Bombycilla cedrorum 1 CATHARTIDAE Turkey vulture Cathartes aura 1 1 1 1 1 1 CHARADRIIDAE Killdeer Charadrius vociferus 1 COLUMBIDAE Mourning dove Zenaida macroura 1 1 1 1 1 1 1 1 1 1 1 1 COLUMBIDAE Band-tailed pigeon Columba fasciata 1 COLUMBIDAE Rock dove (introduced) Columba livia 1 1 1 1 CUCULIDAE Greater roadrunner Geococcyx californianus CORVIDAE American crow Corvus brachyrhinchos 1 1 1 1 1 1 1 1 1 1 1 CORVIDAE Western scrub-jay Aphelocoma californica 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 CORVIDAE Raven Corvus corax 1 EMBERIZIDAE Dark-eyed junco Junco hyemalis 1 1 1 1 1 1 1 EMBERIZIDAE Song sparrow Melospiza melodia 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 EMBERIZIDAE White-crowned sparrow Zonotrichia leucophrys 1 1 1 EMBERIZIDAE California towhee Pipilo crissalis 1 1 1 1 1 1 1 1 1 1 1 1 1 1 EMBERIZIDAE Spotted towhee Pipilo maculatus 1 1 1 1 1 1 1 1 1 1 1 1 1 1 EMBERIZIDAE Yellow warbler Dendroica petechia FALCONIDAE American kestrel Falco sparverius FRINGILLIDAE House finch Carpodactus mexicanus 1 1 1 1 1 1 1 1 1 1 1 1 1 1 FRINGILLIDAE American goldfinch Carduelis tristis 1 1 1 1 FRINGILLIDAE Lesser goldfinch Carduelis lawrencei 1 1 1 1 1 1 1 1 1 1 1 HIRUNDINIDAE Cilff swallow Petrochelidon pyrrhonota 1 1 1 1 1 1 1 HIRUNDINIDAE Northern rough-winged swallow Stelgidopteryx serripennis 1 1 1 1 1 1 1 1 HIRUNDINIDAE Tree swallow Tachycineta bicolor 1

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A3-14 Ecology Consultants, Inc. Table A-3 Vertebrate Species Observed at Streams Study Reaches, 2014

Study Reaches Family Common Name Scientific Name C1 C3 SY3 M1 M2 M3 M4 AB1 AB3 AB5 C1 C3 SJ2 AH1 GAV1 HIRUNDINIDAE Violet-green swallow Trachycineta bicolor 1 1 1 ICTERIDAE Blackbird, red-winged Agelaius phoeniceus 1 ICTERIDAE Bullock's northern oriole Icterus galbula bullockii 1 1 ICTERIDAE Hooded oriole Icterus cucullatus 1 1 LARIDAE Western gull Larus occidentalis 1 1 1 1 1 MIMIDAE Northern mockingbird Mimus polyglottos 1 1 1 1 1 1 1 MIMIDAE California thrasher Toxostoma redivivum 1 ODONTOPHORIDAE California quail Callipepla californica 1 1 PARIDAE Plain oak titmouse Baeolopus inornatus 1 1 1 1 1 1 PARULIDAE Common yellowthroat Geothlypis trichas 1 1 1 1 1 1 1 1 1 1 1 1 1 PASSERIAE House sparrow (introduced) Passer domesticus 1 1 1 PICIDAE Northern flicker Colaptes aurutus 1 1 1 1 1 1 PICIDAE Acorn woodpecker Melanerpes formicivorus 1 1 1 1 1 1 1 1 1 1 PICIDAE Downy woodpecker Picoides pubescens 1 PICIDAE Hairy woodpecker Picoides villosus 1 PODICIPEDIDAE Clark's grebe Aechmophorus clarkii 1 PTILOGONATIDAE Phainopepla Phainopepla nitens 1 1 1 1 RALLIDAE American coot Fulica americana 1 REGULIDAE Ruby-crowned kinglet Regulus calendula 1 STURNIDAE European starling (introduced) Sturnus vulgaris 1 THRAUPIDAE Western tanager Piranga ludoviciana 1 1 1 TIMALIIDAE Wrentit Chamaea fasciata 1 1 1 1 1 1 1 1 1 1 TROCHILIDAE Anna's hummingbird Calypte anna 1 1 1 1 1 1 1 1 1 1 1 1 1 TROCHILIDAE Rufous hummingbird Selasphorus rufus 1 1 1 1 TROGLODYTIDAE Bewick's wren Thryomanes bewickii 1 1 1 1 1 TROGLODYTIDAE Canyon wren Catherpes mexicanus 1 1 1 TURDIDAE American robin Turdus migratorius 1 1 TURDIDAE Hermit thrush Catharus guttatus TURDIDAE Swainson's thrush Catharus ustulatus 1 TYRANNIDAE Pacific-slope flycatcher Empidonax difficilis 1 1 1 1 1 1 1 1 1 TYRANNIDAE Black phoebe Sayornis nigricans 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 TYRANNIDAE Western kingbird Tyrannus verticalis 1 1 TYRANNIDAE Western wood-pewee Contopus sordidulus 1 1 CANIDAE Coyote Canis latrans 1 1 1 1 1 CERVIDAE Mule deer Odocoileus hemionus 1 1 1 1 1 1 1 DIDELPHIDAE Oppossum (introduced) Didelphis virginiana 1 FELIDAE Bobcat Lynx rufus 1 1 1 1 1 LEPORIDAE Cottontail rabbit Sylvilagus auduboni LEPORIDAE Brush rabbit Sylvilagus bachmanni 1 MEPHITIDAE Striped skunk M. mephitis 1 1 PROCYONIDAE Racoon Procyon lotor 1 1 1 1 1 1 1 1 1 1 1 1 1 1 SCIRIDAE Merriam's chipmunk Eutamias merriami 1 SCIRIDAE California ground squirrel Spermophilus beecheyi 1 1 1 SCIRIDAE Western gray squirrel Sciurus griseus 1 TALPIDAE Broad-footed mole Scapanus latimanus 1 1 URSIDAE Black bear Ursus americanus 1 1 # vertebrate species 30 36 26 25 24 29 21 30 35 22 30 36 32 35 35 # native aquatic vertebrate species 2 5 3 2 1 3 4 1 2 1 2 5 3 5 4

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A3-15 Ecology Consultants, Inc. Table A-4: Estuary Study Reach Data ) 2 ) 2 BMIs identified Estuary Year Category Disturbance Class (L,M,X,XX) Salinity Location Survey Date Start Time Air Temp (F) Tide conditions Closed/Open area (acres) watershed wilderness % % herbaceous % urban % agriculture % Disturbed score assessment Habitat Eel grass/pond weed? Algae? Buffer vegetation avg. width (m Vegetation Buffer Native % Width (m) length (m) area surface approx. Maximum depth (m) Dominant substrate RPD depth (cm) Water temp. (c) top Water temp. (c) bottom pH top Dissolved oxygen (mg/l) top Dissolved oxygen (mg/l) bottom Conductivity (mS) top Conductivity (mS) bottom Sp. Cond. (mS) top Sp. Cond. (mS) bottom Salinity (ppt) top Salinity bottom ppt (m) depth Measurement area (m sample BMI (#/m density BMI # BMIs picked # BMIs # AB 1 2012 HIGH DIST X Lower 12-Sep 13:30 75F mid open 6200 49 4 40 7 47 40 3 30 30 400 12000 1.5 sand 0.1 25.8 27.2 8.1 9.3 11.1 19.2 37.1 11.2 22.4 0.7 0.04 165 150 4125 AB 2 2012 HIGH DIST X Upper 12-Sep 13:30 75F mid open 6200 49 4 40 7 47 59 >25 90 10 400 12000 1.5 sand/cobble 0.1 23.6 29.2 8.1 9.4 9.4 4.2 37.2 2.3 21.6 0.7 0.03 165 150 6600 GAV 1 2012 REF M Lower 13-Sep 10:30 70f mid closed 12900 58 40 2 0 2 85 >25 80 40 400 12000 1.5 sand 0.2 21.0 21.0 8.2 7.4 7.4 8.9 8.9 5.5 5.5 0.7 0.08 165 150 1988 GAV 2 2012 REF M Upper 13-Sep 10:30 70f mid closed 12900 58 40 2 0 2 75 >25 80 10 400 12000 1.0 clay none 24.0 24.0 8.2 7.4 7.4 8.9 9.3 5.0 5.3 0.7 0.10 165 150 1650 JAL 1 2012 REF L Lower 13-Sep 8:00 65f high open 16000 75 20 1 4 5 88 >25 80 30 250 7500 1.5 sand 1.0 18.6 19.0 8.2 8.2 8.2 1.4 1.4 0.8 0.8 0.7 0.17 165 150 971 JAL 2 2012 REF L Lower 13-Sep 8:00 65f high open 16000 75 20 1 4 5 88 >25 80 30 250 7500 1.5 sand 1.0 18.6 19.0 8.2 8.2 8.2 1.4 1.4 0.8 0.8 0.7 0.31 165 150 532 MIS 1 2012 HIGH DIST L Lower 12-Sep 9:00 70F low closed 6900 48 0 50 2 52 38 2 10 40 600 18000 1.5 sand 1.0 23.9 23.9 8.1 9.4 9.1 2.2 2.2 1.2 1.2 0.5 0.06 165 150 3000 MIS 2 2012 HIGH DIST L Lower 12-Sep 9:00 70F low closed 6900 48 0 50 2 52 38 2 10 40 600 18000 1.5 sand 0.5 24.2 24.2 8.1 9.7 9.8 2.2 2.2 1.2 1.2 1.0 0.06 165 150 3000 SY 1 2012 HIGH DIST M Lower 12-Sep 11:00 70F low closed 2600 43 0 55 2 57 20 2 60 10 180 1800 1.3 sand 0.5 23.7 23.6 8.2 6.5 6.7 13.0 13.0 7.7 7.7 0.5 0.02 165 150 11000 SY 2 2012 HIGH DIST M Upper 12-Sep 11:00 70F low closed 2600 43 0 55 2 57 20 2 60 10 180 1800 1.3 sand 0.5 24.2 26.1 8.2 6.2 7.8 13.1 17.5 7.7 10.1 0.8 0.06 165 150 3000 TEC 1 2012 MOD DIST L Lower 12-Sep 15:30 75F mid closed 3700 75 2 4 19 23 83 >25 95 12 100 1200 1.3 sand/cobble 0.1 22.4 22.8 7.5 5.1 7.8 3.6 5.0 2.0 2.8 0.6 0.17 165 150 988 TEC 2 2012 MOD DIST L Lower 12-Sep 15:30 75F mid closed 3700 75 2 4 19 23 83 >25 95 12 100 1200 1.3 sand/cobble 0.1 22.4 22.8 7.5 5.1 7.8 3.6 5.0 2.0 2.8 0.6 0.22 165 150 750 AB 1 2013 HIGH DIST X Lower 3-Oct 1600 75 low closed 6200 49 4 40 7 47 40 3 30 30 400 10000 1.5 sand 0.1 25.2 22.1 8.0 12.4 7.0 19.5 39.7 11.6 27.0 0.8 0.19 150 150 789 AB 2 2013 HIGH DIST M Upper 3-Oct 1600 75 low closed 6200 49 4 40 7 47 59 3 30 30 400 10000 1.5 sand/cobble 0.1 21.7 22.1 7.8 12.4 11.4 9.3 12.3 5.6 7.5 0.7 0.18 150 150 833 GAV 1 2013 REF M lower 3-Oct 800 55 high closed 12900 58 40 2 0 2 85 >25 80 30 400 10000 1.5 sand 0.2 14.5 14.8 8.5 7.4 6.5 15.0 15.0 11.2 11.1 0.8 0.05 150 150 3000 GAV 2 2013 MOD DIST M upper 3-Oct 800 55 high closed 12900 58 40 2 0 2 73 >25 80 8 400 10000 1.5 clay 0.1 17.9 19.7 7.6 1.7 1.7 8.5 11.6 5.5 6.6 0.5 0.07 150 150 2143 JAL 2013 REF L lower 3-Oct 1030 65 mid open 16000 75 20 1 4 5 88 >25 80 25 250 6250 1.5 sand 0.1 17.4 17.6 7.8 5.6 5.7 1.6 1.6 0.9 0.9 0.8 0.07 300 300 4286 MIS 1 2013 HIGH DIST L lower 2-Oct 1400 65 low closed 6900 48 0 50 2 52 38 2 10 40 600 15000 1.5 sand none 20.6 20.0 8.1 14.7 14.0 1.9 2.0 1.0 1.1 0.9 0.10 150 150 1500 MIS 2 2013 HIGH DIST L lower 2-Oct 1400 65 low closed 6900 48 0 50 2 52 38 2 10 40 600 15000 1.5 clay 0.1 21.1 20.4 8.1 12.6 11.6 2.0 2.2 1.2 1.2 0.8 0.07 150 150 2143 SY 2013 HIGH DIST X lower 2-Oct 1600 65 low closed 2600 43 0 55 2 57 20 2 60 10 150 1500 1.0 sand 0.1 21.2 20.3 8.4 8.1 6.5 28.4 28.0 19.1 19.2 0.9 0.19 300 300 1579 TEC 2013 MOD DIST L lower 3-Oct 1400 70 low closed 3700 75 2 4 19 23 83 >25 95 10 100 1000 1.2 sand/cobble 0.1 19.6 19.2 7.7 10.9 9.3 3.3 3.3 2.0 2.0 0.7 0.10 300 300 3000 AB 1 2014 HIGH DIST X lower 22-Sep 1500 80 high closed 6200 49 4 40 7 47 40 yes yes 3 30 30 400 10000 1.5 sand none 23.8 31.9 8.0 6.9 7.8 14.0 36.4 14.3 32.3 8.3 20.0 0.8 0.13 150 150 1154 AB 2 2014 HIGH DIST M upper 22-Sep 1630 80 high closed 6200 49 4 40 7 47 59 yes yes >25 90 15 400 10000 1.5 sand/cobble 0.1 24.7 28.6 7.9 11.9 11.2 10.5 26.6 10.6 25.0 6.0 15.1 0.6 0.06 150 150 2500 BELL 2014 MOD DIST XX lower 23-Sep 1300 65 mid closed 3900 75 6 5 14 19 69 no yes 20 60 25 150 3750 1.0 sand 0.5 23.8 23.3 7.7 7.6 7.7 47.0 46.6 48.1 48.3 31.4 31.5 0.6 0.05 150 150 3000 CARP 2014 MOD DIST L lower 22-Sep 1300 80 high closed 9600 80 0 3 17 20 53 no yes 10 60 25 250 6250 1.5 sand 0.1 23.7 23.3 8.1 6.6 6.5 9.1 9.1 9.3 9.3 5.2 5.2 0.6 0.05 150 150 3000 GAV 1 2014 REF X lower 23-Sep 1500 70 mid closed 12900 58 40 2 0 2 85 yes yes >25 80 30 400 10000 1.3 sand 0.1 5.0 21.0 9.0 9.1 7.3 3.0 32.0 34.5 34.5 21.7 21.7 0.6 0.05 150 150 3000 GAV 2 2014 MOD DIST X upper 23-Sep 1700 70 low closed 12900 58 40 2 0 2 70 yes yes 20 80 6 400 10000 0.4 clay 0.1 30.0 27.3 8.8 17.0 15.4 31.6 31.5 28.8 30.2 17.6 18.7 0.3 0.47 28 28 60 GOL 2014 HIGH DIST XX lower 23-Sep 900 65 high closed 30400 53 2 20 25 45 53 no yes 13 50 60 ### 60000 2.0 sand 0.1 22.8 22.8 8.1 2.4 2.6 61.3 61.1 64.0 63.8 43.3 43.2 1.0 0.08 150 150 1923 JAL 1 2014 REF L lower 21-Sep 1700 75 low closed 16000 75 20 1 4 5 85 yes yes >25 80 25 250 6250 1.3 sand 0.1 25.3 25.3 8.3 14.3 13.4 5.4 7.5 2.9 4.2 0.6 0.10 150 150 1500 MIS 2014 HIGH DIST L lower 22-Sep 700 65 low closed 6900 48 0 50 2 52 43 yes yes 4 30 30 600 15000 1.5 sand 0.1 21.5 21.8 8.1 7.8 7.0 7.9 7.9 8.5 8.5 4.7 4.7 0.8 0.05 150 150 3191 MONT 2014 HIGH DIST XX lower 22-Sep 1100 75 mid closed 4500 70 0 29 1 30 18 yes yes 0 0 10 30 300 0.6 sand 0.1 18.6 18.6 8.2 2.4 2.4 56.1 56.1 64.0 63.9 43.3 43.3 0.5 0.11 150 150 1364 SY 2014 HIGH DIST XX lower 22-Sep 830 70 low closed 2600 43 0 55 2 57 23 yes yes 2 20 10 150 1500 1.0 sand 1.0 21.7 21.8 8.1 5.7 5.2 49.3 49.5 52.7 52.7 34.8 34.8 0.8 0.16 150 150 920 TEC 2014 MOD DIST L lower 23-Sep 1100 65 mid closed 3700 75 2 4 19 23 80 yes yes >25 95 10 100 1000 1.0 sand/cobble 0.1 23.9 22.3 7.9 9.8 8.4 6.3 7.1 6.5 7.5 3.5 4.1 0.5 0.47 37 37 79

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A4-16 Ecology Consultants, Inc. Table A-4: Estuary Study Reach Data Emerita a Emerita Estuary # taxa taxa # sens taxa # tol #sens/#tol insects % %non-insects % dominant taxa % 2 dominant taxa % predators %collector-gatherers %pred) - 100+(%cg BMIs Sensitive % % Tolerant BMIs Baetidae Dryopidae Dytiscidae Halipidae Hydrophilidae Ceratopogonidae Chironomidae Culicidae Dolichopodidae Empididae Ephydridae Muscidae Stratiomyidae Corixidae Veliidae Notonectidae Gerridae Aeshnidae Coenagrionidae Lestidae Libeluliidae COLLEMBOLA ACARI GASTROPODA OSTRACODA COPEPODA CLADOCERA DECAPODA-Hippidae- AMPHIPODA-Gammaridea (Shrimp) Mystidacea ISOPODA OLIGOCHAETA POLYCHAETA Bivalvia-clam HIRUDINEA AB 1 5 1 2 0.5 37 63 61 97 35 65 129 1 97 0 0 0 0 0 0 2 0 0 0 0 0 0 53 0 0 0 0 0 0 0 0 0 0 92 1 0 0 2 0 0 0 0 0 0 AB 2 5 1 3 0.3 68 32 65 85 65 35 71 1 95 0 0 0 0 0 0 5 0 0 0 0 0 0 97 0 0 0 0 0 0 0 0 0 0 31 0 0 0 2 0 0 15 0 0 0 GAV 1 8 3 3 1.0 13 87 43 73 5 95 191 56 35 0 0 0 0 0 0 12 0 1 0 0 0 0 6 0 0 0 0 0 0 0 0 0 0 46 0 1 0 65 0 17 0 2 0 0 GAV 2 11 4 3 1.3 77 23 66 80 7 92 185 91 5 99 1 2 0 0 0 4 1 0 0 0 0 0 3 0 0 0 5 1 0 0 0 0 0 2 0 0 0 21 0 11 0 0 0 0 JAL 1 7 4 1 4.0 20 80 56 72 2 98 196 68 16 6 0 0 0 0 0 23 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 2 0 24 0 0 0 0 10 84 0 0 0 0 JAL 2 10 4 3 1.3 25 75 40 58 3 97 194 59 21 10 0 0 0 0 0 24 0 0 0 0 0 0 4 0 0 0 0 0 0 0 0 0 1 27 5 1 0 15 3 60 0 0 0 0 MIS 1 9 2 4 0.5 19 80 46 74 2 93 191 3 75 3 0 1 0 0 0 23 0 1 0 0 0 0 1 0 0 0 0 0 0 0 0 0 7 42 0 69 0 0 0 2 0 0 0 0 MIS 2 11 3 4 0.8 26 74 53 70 5 93 188 11 72 15 0 2 0 0 0 18 0 0 0 0 0 0 1 0 0 0 0 1 0 2 0 1 4 25 0 80 0 0 0 1 0 0 0 0 SY 1 10 3 5 0.6 79 21 43 72 46 54 108 7 64 7 0 3 0 0 0 43 0 0 0 0 0 0 65 0 0 0 0 0 0 1 0 0 0 25 0 1 0 2 0 1 2 0 0 0 SY 2 9 4 4 1.0 50 50 35 62 17 83 165 19 53 8 0 2 0 0 0 41 0 0 0 0 0 0 24 0 0 0 0 0 0 0 0 0 0 52 0 0 0 1 0 8 2 12 0 0 TEC 1 7 2 3 0.7 75 25 41 68 27 72 145 7 51 9 0 0 0 0 0 61 0 0 0 1 0 0 41 0 0 0 0 0 0 0 0 0 0 1 0 35 0 0 0 2 0 0 0 0 TEC 2 10 4 2 2.0 71 29 43 67 23 76 153 8 47 5 0 0 0 0 0 65 0 0 0 1 0 1 34 0 0 0 0 0 0 0 0 1 0 0 1 36 0 1 0 5 0 0 0 0 AB 1 6 2 3 0.7 12 86 69 81 11 86 175 10 87 0 0 0 0 0 0 0 0 0 0 1 0 0 17 0 0 0 0 0 0 0 0 0 0 104 0 0 0 7 0 0 10 8 0 0 AB 2 5 1 3 0.3 93 7 91 95 91 9 17 2 96 0 0 0 0 0 0 3 0 0 0 0 0 0 137 0 0 0 0 0 0 0 0 0 0 6 0 0 0 3 0 0 1 0 0 0 GAV 1 5 3 1 3.0 23 77 53 76 0 100 200 75 3 0 0 0 0 0 0 34 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 4 0 0 0 80 0 14 0 18 0 0 GAV 2 8 1 2 0.5 99 1 39 76 40 60 120 39 38 59 0 0 0 0 0 29 0 0 0 0 0 0 55 1 2 0 0 1 0 2 0 0 0 0 0 0 0 0 0 0 2 0 0 0 JAL 9 3 3 1.0 69 31 43 61 19 67 148 44 31 129 0 0 0 0 0 26 0 0 0 0 0 0 53 0 0 0 0 0 0 0 0 3 44 24 4 16 0 0 0 1 0 0 0 0 MIS 1 10 3 4 0.8 36 64 33 51 20 70 150 25 55 10 0 2 0 0 0 14 0 0 0 0 0 0 28 0 0 0 0 0 0 0 0 0 15 49 1 3 0 2 0 26 0 0 0 0 MIS 2 10 2 3 0.7 12 88 60 83 1 77 176 7 63 7 0 0 0 0 0 10 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 34 90 0 4 0 0 0 4 0 0 0 0 SY 6 2 3 0.7 56 44 56 95 56 44 88 2 95 0 0 0 0 0 0 0 0 0 0 0 0 0 168 0 0 0 0 0 0 0 0 0 0 117 8 0 0 0 0 3 1 3 0 0 TEC 10 3 3 1.0 69 31 46 66 7 93 187 24 28 50 0 0 0 0 0 138 0 0 0 0 0 0 18 0 0 0 0 1 0 1 0 0 0 60 3 0 0 10 0 13 6 0 0 0 AB 1 8 2 4 0.5 95 5 78 92 79 21 41 1 83 1 0 2 0 0 0 21 2 0 0 0 0 0 117 0 0 0 0 0 0 0 0 0 0 4 0 0 0 1 0 0 2 0 0 0 AB 2 10 4 3 1.3 57 43 41 67 41 59 117 9 80 8 0 0 0 0 0 14 1 0 0 0 0 0 61 0 0 0 1 0 0 0 0 0 0 40 1 0 0 4 0 1 19 0 0 0 BELL 4 1 1 1.0 99 1 80 95 95 1 7 1 80 0 0 0 0 0 22 0 0 0 0 6 0 0 120 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 CARP 9 3 3 1.0 52 48 38 68 7 93 187 31 48 44 0 3 0 0 0 25 0 0 0 0 0 0 0 0 0 0 0 4 0 2 0 1 0 12 0 0 0 0 0 2 57 0 0 0 GAV 1 7 4 2 2.0 4 96 41 69 1 99 199 55 42 0 0 0 0 0 0 5 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 62 0 0 0 15 6 42 0 19 0 0 GAV 2 3 0 2 0.0 93 7 64 93 29 71 143 0 36 0 0 0 0 0 0 18 0 0 0 0 0 0 8 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 GOL 4 2 2 1.0 18 82 56 74 18 82 164 70 30 0 0 0 0 0 0 0 0 0 0 0 0 0 27 0 0 0 0 0 0 0 0 0 0 18 0 0 0 84 0 0 0 21 0 0 JAL 1 11 4 5 0.8 50 56 43 71 11 87 177 25 53 33 0 1 0 0 0 29 0 0 0 0 0 0 11 0 0 0 1 0 0 0 0 3 12 64 0 3 0 0 1 0 1 0 0 0 MIS 9 2 4 0.5 36 64 41 62 10 80 170 5 63 7 0 11 0 0 0 32 0 0 0 0 0 0 3 0 0 0 0 0 0 1 0 0 15 61 0 0 0 0 0 1 19 0 0 0 MONT 5 1 2 0.5 23 87 77 97 1 89 187 9 78 0 0 0 0 0 1 3 0 0 0 29 0 0 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 116 14 0 0 SY 6 2 1 2.0 17 73 71 88 17 73 155 73 17 0 0 0 0 0 0 0 0 0 0 0 0 0 26 0 0 0 0 0 0 0 0 0 0 0 0 0 0 106 0 3 0 0 1 0 TEC 5 0 2 0.0 30 70 32 59 3 84 181 0 57 0 0 0 0 1 0 10 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 5 9 0 0 0 0 0 0 12 0 0 0

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A4-17 Ecology Consultants, Inc. Table A-5 Streams BMIs Tolerance Values and ANOVA Summary

CLASS ORDER Family r-square p Group n Mean Std Error Lower 95% Upper 95% Updated TV Previous TV INSECTA EPHEMEROPTERA Baetidae 0.001 0.9027 HIGH DIST 106 57.9528 5.4121 47.282 68.624 5 5 (Insects) (Mayflies) MOD DIST 53 58.5849 7.6538 43.494 73.676 REF 48 62.2708 8.0426 46.414 78.128 Caenidae 0.2092 <0.0001 HIGH DIST 106 0.7736 1.1766 -1.55 3.094 3 2 MOD DIST 53 11.3962 1.664 8.12 14.677 REF 48 14.6458 1.7485 11.2 18.093 Emphemerellidae 0.0929 <0.0001 HIGH DIST 106 0.00943 0.30169 -0.585 0.6043 1 1 MOD DIST 53 0.4717 0.42665 -0.37 1.3129 REF 48 2.45833 0.44832 1.574 3.3423 Heptagenidae 0.4111 <0.0001 HIGH DIST 106 0.1509 0.47519 -0.786 1.088 0 0 MOD DIST 53 1.3962 0.67201 0.071 2.721 REF 48 10.1042 0.70615 8.712 11.496 Leptohyphidae 0.1109 <0.0001 HIGH DIST 106 0.87736 1.0074 -1.109 2.864 2 2 MOD DIST 53 8.84906 1.4247 6.04 11.658 REF 48 7.1875 1.4971 4.236 10.139 Leptophlebiidae 0.3424 <0.0001 HIGH DIST 106 0.5566 1.1119 -1.64 2.749 2 2 MOD DIST 53 10.3208 1.5725 7.22 13.421 REF 48 20.7292 1.6524 17.47 23.987 PLECOPTERA Chloroperlidae 0.1897 <0.0001 HIGH DIST 106 0 0.25293 -0.499 0.4987 0 0 (Stoneflies) MOD DIST 53 0.11321 0.35769 -0.592 0.8185 REF 48 3 0.37586 2.259 3.7411 Nemouridae 0.2 <0.0001 HIGH DIST 106 0.14151 0.49724 -0.839 1.1219 0 0 MOD DIST 53 1.92453 0.70321 0.538 3.311 REF 48 6.5 0.73893 5.043 7.9569 Perlidae 0.1899 <0.0001 HIGH DIST 106 0.00943 0.11439 -0.216 0.235 0 0 MOD DIST 53 0.01887 0.16177 -0.3 0.3378 REF 48 1.35417 0.16999 1.019 1.6893 Perlodidae 0.062942 0.0013 HIGH DIST 106 0 0.07121 -0.1404 0.14041 NA 2 MOD DIST 53 0.396226 0.10071 0.1977 0.59479 REF 48 0.354167 0.10582 0.1455 0.56282 TRICHOPTERA Brachycentridae 0.0768 0.0003 HIGH DIST 106 0.33962 0.29841 -0.249 0.928 3 3 (Caddisflies) MOD DIST 53 1.03774 0.42202 0.206 1.8698 REF 48 2.54167 0.44345 1.667 3.416 Glossostomatidae 0.0874 <0.0001 HIGH DIST 106 0.06604 0.21244 -0.353 0.4849 3 3 MOD DIST 53 1.13208 0.30043 0.54 1.7244 REF 48 1.625 0.31569 1.003 2.2474 Helicopsychidae 0.16929 <0.0001 HIGH DIST 106 0.03774 0.14447 -0.247 0.3226 1 1 MOD DIST 53 0 0.20431 -0.403 0.4028 REF 48 1.60417 0.21469 1.181 2.0275 Hydropsychidae 0.06839 0.0007 HIGH DIST 106 1.88679 0.49457 0.9117 2.8619 5 5 MOD DIST 53 5.07547 0.69942 3.6964 6.4545 REF 48 2.0625 0.73495 0.6134 3.5116 Hydroptilidae 0.0075 0.4632 HIGH DIST 106 1.5 0.31489 0.8792 2.1208 5 5

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A5-18 Ecology Consultants, Inc. Table A-5 Streams BMIs Tolerance Values and ANOVA Summary

MOD DIST 53 0.96226 0.44532 0.0843 1.8403 REF 48 0.91667 0.46794 -0.0059 1.8393 Lepidostomatidae 0.3591 <0.0001 HIGH DIST 106 0.1509 0.7504 -1.33 1.631 2 2 MOD DIST 53 3.8679 1.0613 1.78 5.96 REF 48 14.5 1.1152 12.3 16.699 Leptoceridae 0.041017 0.014 HIGH DIST 106 0 0.02698 -0.0532 0.0532 NA 4 MOD DIST 53 0.132075 0.03816 0.0568 0.20731 REF 48 0.083333 0.0401 0.0043 0.16239 Limnephillidae 0.107685 <0.0001 HIGH DIST 106 0.009434 0.03394 -0.0575 0.07635 NA 4 MOD DIST 53 0 0.048 -0.0946 0.09463 REF 48 0.291667 0.05043 0.1922 0.39111 Odontoceridae - - HIGH DIST 106 0 0 0 0 NA 0 MOD DIST 53 0 0 0 0 REF 48 0 0 0 0 Philopotamidae 0.0001 0.9888 Level Number Mean Std Error Lower 95% Upper 95% 5 5 HIGH DIST 106 1.43396 0.36694 0.71048 2.1574 MOD DIST 53 1.33962 0.51893 0.31646 2.3628 REF 48 1.41667 0.54529 0.34153 2.4918 Polycentropodidae 0.1717 <0.0001 HIGH DIST 106 0.06604 0.11828 -0.167 0.2992 2 2 MOD DIST 53 0.73585 0.16727 0.406 1.0656 REF 48 1.41667 0.17576 1.07 1.7632 Psychomyiidae 0.077 0.0003 HIGH DIST 106 0.056604 0.12465 -0.1892 0.3024 NA 5 MOD DIST 53 0.943396 0.17628 0.5958 1.291 REF 48 0.270833 0.18523 -0.0944 0.636 Rhyacophilidae 0.32 <0.0001 HIGH DIST 106 0.14151 0.2092 -0.271 0.554 2 2 MOD DIST 53 1.35849 0.29586 0.775 1.9418 REF 48 3.8125 0.31088 3.2 4.4255 Sericostomatidae 0.1184 <0.0001 HIGH DIST 106 0.61321 0.49035 -0.354 1.58 3 3 MOD DIST 53 4.22642 0.69346 2.859 5.5937 REF 48 4.35417 0.72869 2.917 5.7909 COLEOPTERA Carabidae 0.01608 0.1914 HIGH DIST 106 0 0.00673 -0.0133 0.01327 NA 4 (Beetles) MOD DIST 53 0 0.00952 -0.0188 0.01876 REF 48 0.020833 0.01 0.0011 0.04055 Dryopidae 0.028439 0.0527 HIGH DIST 106 0.009434 0.05108 -0.0913 0.11014 NA 5 MOD DIST 53 0.188679 0.07224 0.0463 0.3311 REF 48 0.1875 0.0759 0.0378 0.33716 Dytisidae 0.02742 0.0587 HIGH DIST 106 3.5566 0.59425 2.3849 4.7283 5 5 MOD DIST 53 5.81132 0.8404 4.1543 7.4683 REF 48 5.29167 0.88309 3.5505 7.0328 Elmidae 0.22028 <0.0001 HIGH DIST 106 1.0283 0.6863 -0.325 2.382 0 0 MOD DIST 53 4.2642 0.9706 2.35 6.178 REF 48 10.3542 1.0199 8.343 12.365 Gyrinidae 0.004957 0.6024 HIGH DIST 106 0.056604 0.02093 0.0153 0.09786 NA 5 MOD DIST 53 0.056604 0.02959 -0.0017 0.11495

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A5-19 Ecology Consultants, Inc. Table A-5 Streams BMIs Tolerance Values and ANOVA Summary

REF 48 0.020833 0.0311 -0.0405 0.08215 Halipidae 0.039143 0.017 HIGH DIST 106 1.77358 0.29528 1.191 2.3558 9 9 MOD DIST 53 1.24528 0.41759 0.422 2.0686 REF 48 0.25 0.4388 -0.615 1.1152 Hydrophilidae 0.023683 0.0867 HIGH DIST 106 0.358491 0.08909 0.1828 0.53414 NA 5 MOD DIST 53 0.113208 0.12599 -0.1352 0.36161 REF 48 0.041667 0.13239 -0.2194 0.30269 Psphenidae 0.1268 <0.0001 HIGH DIST 106 0.16038 0.45125 -0.729 1.0501 2 2 MOD DIST 53 2.50943 0.63816 1.251 3.7677 REF 48 4.41667 0.67058 3.095 5.7388 DIPTERA Blephariceridae 0.05945 0.0019 HIGH DIST 106 0 0.05244 -0.1034 0.10339 NA 0 (True flies) MOD DIST 53 0.150943 0.07416 0.0047 0.29716 REF 48 0.333333 0.07792 0.1797 0.48697 Ceratopogonidae 0.001248 0.8804 HIGH DIST 106 2.81132 0.62277 1.5834 4.0392 5 5 MOD DIST 53 2.67925 0.88073 0.9427 4.4158 REF 48 2.25 0.92547 0.4253 4.0747 Chironomidae 0.1368 <0.0001 HIGH DIST 106 115.906 5.4018 105.26 126.56 8 8 MOD DIST 53 74.887 7.6393 59.82 89.95 REF 48 69.042 8.0273 53.21 84.87 Culicidae 0.018399 0.1504 HIGH DIST 106 0.169811 0.1866 -0.1981 0.5377 NA 8 MOD DIST 53 0.735849 0.26389 0.2156 1.2561 REF 48 0.083333 0.27729 -0.4634 0.6301 Dixidae 0.159879 <0.0001 Level Number Mean Std Error Lower 95% Upper 95% 3 3 HIGH DIST 106 0.075472 0.07936 -0.081 0.2319 MOD DIST 53 0.415094 0.11223 0.1938 0.6364 REF 48 0.958333 0.11793 0.7258 1.1909 Dolichopodidae 0.001913 0.8225 HIGH DIST 106 0.009434 0.01168 -0.0136 0.03247 NA 4 MOD DIST 53 0.018868 0.01652 -0.0137 0.05144 REF 48 0.020833 0.01736 -0.0134 0.05506 Empididae 0.004423 0.6363 HIGH DIST 106 0.358491 0.06885 0.22274 0.49424 NA 6 MOD DIST 53 0.245283 0.09737 0.05331 0.43726 REF 48 0.3125 0.10231 0.11077 0.51423 Ephydridae 0.022524 0.0979 HIGH DIST 106 0.641509 0.16535 0.3155 0.96753 NA 6 MOD DIST 53 0.415094 0.23385 -0.046 0.87616 REF 48 0 0.24572 -0.4845 0.48449 Muscidae 0.018457 0.1495 HIGH DIST 106 0.188679 0.04204 0.1058 0.27157 NA 6 MOD DIST 53 0.132075 0.05945 0.0149 0.2493 REF 48 0.041667 0.06247 -0.0815 0.16484 Psychodidae 0.019985 0.1276 HIGH DIST 106 0.69811 0.20585 0.2922 1.104 5 5 MOD DIST 53 0.56604 0.29112 -0.008 1.14 REF 48 1.35417 0.30591 0.751 1.9573 Sciomyzidae 0.004625 0.6232 HIGH DIST 106 0.009434 0.00677 -0.0039 0.02278 NA 6 MOD DIST 53 0 0.00957 -0.0189 0.01887 REF 48 0 0.01006 -0.0198 0.01983

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A5-20 Ecology Consultants, Inc. Table A-5 Streams BMIs Tolerance Values and ANOVA Summary

Simulidae 0.0362 0.0233 HIGH DIST 106 21.4434 2.3854 16.74 26.147 7 7 MOD DIST 53 19.1321 3.3734 12.481 25.783 REF 48 9.7083 3.5448 2.719 16.697 Stratiomyidae 0.041882 0.0127 HIGH DIST 106 0.63208 0.8361 -1.016 2.2806 3 3 MOD DIST 53 4.58491 1.1824 2.254 6.9162 REF 48 3.66667 1.2425 1.217 6.1164 Tipulidae 0.138709 <0.0001 HIGH DIST 106 1.23585 0.28246 0.6789 1.7928 1 1 MOD DIST 53 1.11321 0.39946 0.3256 1.9008 REF 48 3.9375 0.41975 3.1099 4.7651 HEMIPTERA Belostomatidae 0.0528 0.004 HIGH DIST 106 0.150943 0.06461 0.02355 0.27833 NA 8 (True bugs) MOD DIST 53 0.528302 0.09137 0.34814 0.70846 REF 48 0.270833 0.09602 0.08152 0.46014 Corixidae 0.004299 0.6444 HIGH DIST 106 0.207547 0.1212 -0.0314 0.44652 NA 8 MOD DIST 53 0.264151 0.1714 -0.0738 0.6021 REF 48 0.041667 0.18011 -0.3135 0.39678 Gerridae 0.015916 0.1947 HIGH DIST 106 0.075472 0.03519 0.00608 0.14486 NA 5 MOD DIST 53 0.132075 0.04977 0.03394 0.23021 REF 48 0.1875 0.0523 0.08438 0.29062 Naucoridae 0.045905 0.0083 HIGH DIST 106 0 0.22773 -0.449 0.449 5 5 MOD DIST 53 1.16981 0.32206 0.5348 1.8048 REF 48 0 0.33842 -0.6673 0.6673 Veliidae 0.082137 0.0002 HIGH DIST 106 0.14151 0.12594 -0.1068 0.3898 3 3 MOD DIST 53 0.62264 0.17811 0.2715 0.9738 REF 48 1.08333 0.18716 0.7143 1.4523 ODONATA Aeshidae 0.036484 0.0226 HIGH DIST 106 0.35849 0.15834 0.04631 0.6707 3 3 (Dragonflies and MOD DIST 53 0.86792 0.22392 0.42643 1.3094 Damselflies) REF 48 1.08333 0.23529 0.61941 1.5473 Calypterygidae 0.014105 0.2348 HIGH DIST 106 0 0.04042 -0.0797 0.07969 NA 5 MOD DIST 53 0.113208 0.05716 0.00052 0.2259 REF 48 0 0.06006 -0.1184 0.11842 Coenagrionidae 0.012786 0.2691 HIGH DIST 106 2 0.31512 1.3787 2.6213 5 5 MOD DIST 53 1.67925 0.44564 0.8006 2.5579 REF 48 1.08333 0.46828 0.1601 2.0066 Cordulegastridae 0.115686 <0.0001 HIGH DIST 106 0.075472 0.09117 -0.1043 0.2552 3 3 MOD DIST 53 0.396226 0.12894 0.142 0.6504 REF 48 0.916667 0.13548 0.6495 1.1838 Gomphidae 0.1507 <0.0001 HIGH DIST 106 0.00943 0.16812 -0.322 0.3409 0 0 MOD DIST 53 0.26415 0.23776 -0.205 0.7329 REF 48 1.79167 0.24984 1.299 2.2843 Lestidae 0.07614 0.0003 HIGH DIST 106 0.40566 0.18469 0.0415 0.7698 5 5 MOD DIST 53 1.71698 0.26119 1.202 2.232 REF 48 0.8125 0.27446 0.2714 1.3536 Libellulidae 0.03103 0.0401 HIGH DIST 106 0.056604 0.05286 -0.0476 0.16083 NA 9 MOD DIST 53 0.226415 0.07476 0.079 0.37381

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A5-21 Ecology Consultants, Inc. Table A-5 Streams BMIs Tolerance Values and ANOVA Summary

REF 48 0.270833 0.07855 0.116 0.42571 MEGALOPTERA Corydalidae 0.054899 0.0032 HIGH DIST 106 0.037736 0.03497 -0.0312 0.10669 NA 0 (Alderflies) MOD DIST 53 0.226415 0.04946 0.1289 0.32392 REF 48 0.1875 0.05197 0.085 0.28996 Sialidae 0.098551 <0.0001 HIGH DIST 106 0.16038 0.21662 -0.267 0.5875 4 3 MOD DIST 53 1.90566 0.30635 1.302 2.5097 REF 48 1.04167 0.32191 0.407 1.6764 COLLEMBOLA 0.0076 0.4558 HIGH DIST 106 0.160377 0.06298 0.0362 0.28456 NA 10 (Springtails) MOD DIST 53 0.09434 0.08907 -0.0813 0.26996 REF 48 0.020833 0.0936 -0.1637 0.20537 ARACHNIDA ACARI 0.065018 0.0011 HIGH DIST 106 1 0.33311 0.3432 1.6568 3 3 (Water mites) MOD DIST 53 1.43396 0.47109 0.5051 2.3628 REF 48 3.22917 0.49502 2.2532 4.2052 GASTROPODA 0.034263 0.0286 HIGH DIST 106 11.2358 1.9416 7.408 15.064 7 5 (Snails) MOD DIST 53 5.4906 2.7458 0.077 10.904 REF 48 2.4792 2.8853 -3.21 8.168 OSTRACODA 0.041988 0.0126 HIGH DIST 106 15.3962 2.8175 9.84 20.951 7 7 (Seed shrimp) MOD DIST 53 20.7547 3.9845 12.9 28.611 REF 48 3.8958 4.1869 -4.36 12.151 COPEPODA 0.057403 0.0024 HIGH DIST 106 5.31132 0.8821 3.572 7.0506 7 7 MOD DIST 53 1.67925 1.2475 -0.78 4.1389 REF 48 0.20833 1.3109 -2.376 2.7929 BRANCHIPODA CLADOCERA 0.045811 0.0084 HIGH DIST 106 12.1415 2.6902 6.837 17.446 9 9 (Water fleas) MOD DIST 53 0.1698 3.8045 -7.331 7.671 REF 48 0 3.9978 -7.882 7.882 MALACOSTRACA DECAPODA 0.039136 0.017 HIGH DIST 106 0.132075 0.03201 0.069 0.19518 NA 8 (Crayfish) MOD DIST 53 0 0.04526 -0.0892 0.08924 REF 48 0 0.04756 -0.0938 0.09378 AMPHIPODA 0.009687 0.3705 HIGH DIST 106 1.33019 0.59224 0.162 2.4979 5 5 MOD DIST 53 1.54717 0.83755 -0.104 3.1985 REF 48 0 0.8801 -1.735 1.7353 ISOPODA 0.036546 0.0224 HIGH DIST 106 6.67925 1.6574 3.411 9.947 9 8 MOD DIST 53 0.03774 2.3439 -4.584 4.6591 REF 48 0.125 2.4629 -4.731 4.9811 OLIGOCHAETA 0.076401 0.0003 HIGH DIST 106 10.8019 1.3908 8.06 13.544 9 9 (segmented worms) MOD DIST 53 3.3585 1.9668 -0.519 7.236 REF 48 1.9375 2.0667 -2.137 6.012 HIRUDINEA 0.037141 0.0211 HIGH DIST 106 0.471698 0.10279 0.269 0.67437 NA 10 (Leeches) MOD DIST 53 0.132075 0.14537 -0.1545 0.4187 REF 48 0 0.15276 -0.3012 0.30118 TURBELLARIA 0.013214 0.2575 HIGH DIST 106 0.764151 0.18072 0.4078 1.1205 NA 4 (Flat worms) MOD DIST 53 0.603774 0.25558 0.0999 1.1077 REF 48 0.229167 0.26856 -0.3003 0.7587

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A5-22 Ecology Consultants, Inc. Table A-6 Stream BMI Metric ANOVAs Summary

Parameter r-square p Group n Mean Std Error Lower 95% Upper 95% # EPT families 0.653212 <0.0001 HIGH DIST 106 2.9151 0.28674 2.35 3.48 MOD DIST 53 8.3774 0.40551 7.578 9.177 REF 48 12.625 0.42611 11.785 13.465 % sens BMIs 0.602894 <0.0001 HIGH DIST 106 3.038 1.282 0.51 5.566 MOD DIST 53 23.2068 1.8131 19.632 26.782 REF 48 42.5285 1.9052 38.772 46.285 TV Avg. 0.593264 <0.0001 HIGH DIST 106 6.93698 0.08626 6.7669 7.1071 MOD DIST 53 5.55132 0.12199 5.3108 5.7918 REF 48 4.34792 0.12818 4.0952 4.6006 %EPT - Baetidae 0.565937 <0.0001 HIGH DIST 106 3.0171 1.0964 0.855 5.179 MOD DIST 53 19.9807 1.5506 16.924 23.038 REF 48 34.0388 1.6293 30.826 37.251 # insect families 0.53722 <0.0001 HIGH DIST 106 10.6321 0.53705 9.573 11.691 MOD DIST 53 19.4151 0.7595 17.918 20.913 REF 48 24.625 0.79808 23.051 26.199 % sh+pred 0.452963 <0.0001 HIGH DIST 106 4.9065 0.59643 3.731 6.082 MOD DIST 53 11.9311 0.84348 10.268 13.594 REF 48 18.4492 0.88632 16.702 20.197 %PT 0.451545 <0.0001 HIGH DIST 106 2.193 0.58039 1.049 3.337 MOD DIST 53 8.1746 0.82079 6.556 9.793 REF 48 15.5167 0.86248 13.816 17.217 % tol BMIs 0.420505 <0.0001 HIGH DIST 106 70.8208 1.9733 66.93 74.711 MOD DIST 53 46.1321 2.7907 40.63 51.634 REF 48 29.8333 2.9324 24.052 35.615 %sh 0.400024 <0.0001 HIGH DIST 106 0.35402 0.39795 -0.431 1.1387 MOD DIST 53 3.69639 0.56279 2.587 4.806 REF 48 8.62509 0.59138 7.459 9.7911 % non-insects + dipt0.391048 <0.0001 HIGH DIST 106 73.2999 1.9536 69.448 77.152 MOD DIST 53 50.387 2.7628 44.94 55.834 REF 48 35.0959 2.9031 29.372 40.82 % non-insects+chiro 0.337586 <0.0001 HIGH DIST 106 63.4603 2.1049 59.31 67.61 MOD DIST 53 39.794 2.9768 33.925 45.663 REF 48 27.5078 3.128 21.34 33.675 %EPT 0.318241 <0.0001 HIGH DIST 106 22.775 1.9049 19.019 26.531 MOD DIST 53 40.7579 2.6939 35.446 46.069 REF 48 54.913 2.8307 49.332 60.494 %sc+sh+pred 0.21997 <0.0001 HIGH DIST 106 8.944 0.991 6.99 10.898 MOD DIST 53 15.7849 1.4014 13.022 18.548 REF 48 22.0672 1.4726 19.164 24.971 %pred 0.209773 <0.0001 HIGH DIST 106 4.52867 0.43953 3.6621 5.395 MOD DIST 53 8.31152 0.62158 7.086 9.537 REF 48 9.83479 0.65316 8.547 11.123 % Coleoptera 0.181011 <0.0001 HIGH DIST 106 1.5962 0.32372 0.9579 2.2345 MOD DIST 53 3.77218 0.45781 2.8695 4.6748 REF 48 5.32927 0.48106 4.3808 6.2778 % diptera 0.142359 <0.0001 HIGH DIST 106 49.7043 1.9295 45.9 53.509 MOD DIST 53 37.3814 2.7287 32.001 42.762 REF 48 30.8689 2.8673 25.216 36.522

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A5-23 Ecology Consultants, Inc. Table A-6 Stream BMI Metric ANOVAs Summary

% chironomidae 0.138286 <0.0001 HIGH DIST 106 39.8646 1.8245 36.267 43.462 MOD DIST 53 26.7884 2.5803 21.701 31.876 REF 48 23.2809 2.7113 17.935 28.627 % non-insects 0.136176 <0.0001 HIGH DIST 106 23.5957 1.9687 19.71 27.477 MOD DIST 53 13.0056 2.7841 7.52 18.495 REF 48 4.227 2.9256 -1.54 9.995 %sc+sh 0.121295 <0.0001 HIGH DIST 106 4.4153 0.8255 2.7877 6.043 MOD DIST 53 7.4734 1.1674 5.1716 9.775 REF 48 12.2324 1.2267 9.8137 14.651 %cg+sc+sh 0.09333 <0.0001 HIGH DIST 106 44.5779 1.8913 40.849 48.307 MOD DIST 53 53.7571 2.6747 48.483 59.031 REF 48 59.2656 2.8106 53.724 64.807 %cg+pred 0.080683 0.0002 HIGH DIST 106 44.6913 1.8321 41.079 48.304 MOD DIST 53 54.5952 2.591 49.487 59.704 REF 48 56.868 2.7226 51.5 62.236 % cf 0.041278 0.0136 HIGH DIST 106 8.71077 0.8583 7.0184 10.403 MOD DIST 53 9.00624 1.2139 6.6129 11.4 REF 48 4.5057 1.2755 1.9908 7.021 %cg 0.028803 0.0507 HIGH DIST 106 40.1626 1.8454 36.524 43.801 MOD DIST 53 46.2837 2.6099 41.138 51.429 REF 48 47.0332 2.7424 41.626 52.44 %cg+cf 0.018502 0.1488 HIGH DIST 106 48.8734 1.8958 45.136 52.611 MOD DIST 53 55.2899 2.681 50.004 60.576 REF 48 51.5389 2.8172 45.984 57.093 BMI density 0.000814 0.9203 HIGH DIST 106 1114.55 116.24 885.35 1343.7 MOD DIST 53 1096.71 164.39 772.59 1420.8 REF 48 1030.17 172.74 689.58 1370.8 %sc 0.000735 0.9277 HIGH DIST 106 4.06129 0.6918 2.6973 5.4253 MOD DIST 53 3.77702 0.9783 1.848 5.706 REF 48 3.60729 1.028 1.5803 5.6342

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A5-24 Ecology Consultants, Inc. Table A-7 Summary of Mulitple Regression Analyses: Physiochemical Parameters vs. Disturbance Regressors, Test Group Data (n=207)

Physiochemical Parameter (y) Disturbance Regressor (xr-square p Relationship with Disturbance Elevation whole model 0.4655 <0.0001 negative Habitat Score <0.0001 % disturbed 0.0602 Gradient whole model 0.5041 <0.0001 negative Habitat Score <0.0001 % disturbed 0.3876 Watershed area whole model 0.206 <0.0001 positive Habitat Score <0.0001 % disturbed <0.0001 Stream temperature whole model 0.2545 <0.0001 positive Habitat Score <0.0001 % disturbed 0.2093 Dissolved oxygen whole model 0.0013 0.8763 none Habitat Score 0.63 % disturbed 0.6284 Specific conductivity whole model 0.3711 <0.0001 positive Habitat Score 0.0506 % disturbed <0.0001

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A7-25 Ecology Consultants, Inc. Table A-8 Summary of Linear Regression Analyses of Potential Core Metrics vs. Physiochemical Regressors, REF data (n=58)

Indicator Metric (y) Regressor (x) r-square p linear fit p < 0.05? relationship w/regresso relationship w/DISTregressor/DIST relationshi confound? # EPT families elevation 0.042983 0.1184 # EPT families = 13.674662 - 0.0018994*Elevation (ft.) no negative no gradient 0.024075 0.2448 # EPT families = 13.540714 - 13.501724*Gradient no negative no wshed area 0.097892 0.0168 # EPT families = 10.218386 + 0.000861*watershed area yes positive negative positive no stream temp 0.001693 0.7591 # EPT families = 11.782267 + 0.0585562*Stream temp. (c) no positive no conductivity 0.000258 0.9091 # EPT families = 13.080194 - 0.0004282*Conductivity (microS)no negative no overall NO % sens BMIs elevation 0.027927 0.2099 % sens BMIs = 46.821016 - 0.0084585*Elevation (ft.) no negative no gradient 0.007276 0.5244 % sens BMIs = 44.995023 - 41.008361*Gradient no negative no wshed area 0.004654 0.6109 % sens BMIs = 39.40162 + 0.0010371*watershed area no negative no stream temp 0.053002 0.0821 % sens BMIs = 14.838406 + 1.8102944*Stream temp. (c) no positive no conductivity 0.068317 0.0587 % sens BMIs = 17.767196 + 0.0383657*Conductivity (microS) no positive no overall NO Tolerance Value Avg. elevation 0.062378 0.0587 Tolerance Value Avg. = 3.9350822 + 0.0006668*Elevation (ft.) no positive no gradient 0.001687 0.7595 Tolerance Value Avg. = 4.2199766 + 1.0415215*Gradient no positive no wshed area 0.00183 0.7498 Tolerance Value Avg. = 4.3847548 - 3.4312e-5*watershed are no negative no stream temp 0.087521 0.0242 Tolerance Value Avg. = 6.152376 - 0.1227121*Stream temp. yes negative positive positive no conductivity 0.056905 0.0854 Tolerance Value Avg. = 5.3197721 - 0.0017139*Conductivity ( no negative no overall NO %EPT-Baetidae elevation 0.060769 0.0621 %EPT - Baetidae = 39.149493 - 0.0103735*Elevation (ft.) no negative no gradient 0.026807 0.2194 %EPT - Baetidae = 37.884241 - 65.440367*Gradient no negative no wshed area 0.005521 0.5794 %EPT - Baetidae = 30.998831 + 0.0009392*watershed area no positive no stream temp 0.010049 0.454 %EPT - Baetidae = 23.713837 + 0.6553203*Stream temp. (c) no positive no conductivity 0.09048 0.0286 %EPT - Baetidae = 9.0905263 + 0.0374621*Conductivity (mic yes positive negative positive no overall NO # insect families elevation 0.001287 0.7892 # insect families = 25.400753 - 0.0005308*Elevation (ft.) no negative no gradient 0.013946 0.3773 # insect families = 24.053512 + 16.594183*Gradient no positive no wshed area 0.002812 0.6926 # insect families = 24.448997 + 0.0002357*watershed area no positive no stream temp 0.055349 0.0754 # insect families = 16.901094 + 0.5407062*Stream temp. (c) no positive no conductivity 0.030075 0.2143 # insect families = 20.19683 + 0.0075698*Conductivity (micro no positive no overall NO % sh+pred elevation 0.009562 0.5406 % sh+pred = 17.43226 + 0.0021072*Elevation (ft.) no positive no gradient 0.058875 0.0665 % sh+pred = 15.350205 + 49.664689*Gradient no positive no wshed area 0.054083 0.079 % sh+pred = 22.834694 - 0.0015053*watershed area no negative no stream temp 0.006655 0.3752 % sh+pred = 14.392601 + 0.2731002*Stream temp. (c) no positive no conductivity 0.11016 0.0152 % sh+pred = 5.1441309 + 0.0208154*Conductivity (microS) yes positive negative positive no overall NO %PT elevation 0.012539 0.7111 % PT = 17.164684 - 0.0027693*Elevation (ft.) no negative no gradient 0.007669 0.5333 % PT = 14.380541 + 20.57051*Gradient no positive no wshed area 0.027391 0.2144 % PT = 19.20748 - 0.0012294*watershed area no negative no stream temp 0.000324 0.8933 % PT = 14.651809 + 0.0691788*Stream temp. (c) no positive no conductivity 0.084477 0.0347 % PT = 1.9493697 + 0.0210651*Conductivity (microS) yes positive negative positive no overall NO %tol BMIs elevation 0.10984 0.011 % tol BMIs = 20.389162 + 0.015304*Elevation (ft.) yes positive positive negative no gradient 0.018723 0.3057 % tol BMIs = 24.605048 + 60.013925*Gradient no positive no wshed area 0.010684 0.44 % tol BMIs = 32.550817 - 0.0014336*watershed area no negative no stream temp 0.07722 0.0347 % tol BMIs = 58.768293 - 1.9934576*Stream temp. (c) yes negative positive positive no conductivity 0.003891 0.6572 % tol BMIs = 30.399727 - 0.0069238*Conductivity (microS) no negative no overall NO overall NO

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Table A8-26 Ecology Consultants, Inc. Table A-9 Correlations Between Potential Core BMI Metrics

Indicator Metric # EPT families% sens BMIs Tolerance Value Avg%EPT-Baetidae# insect families% sh+pred %PT %tol BMIs # EPT families 1 0.7133 0.6983 0.7083 0.8671 0.5635 0.6225 0.5272 % sens BMIs 0.7133 1 0.7978 0.927 0.6148 0.6205 0.6402 0.4952 Tolerance Value Avg. 0.6983 0.7978 1 0.7623 0.6221 0.5287 0.5509 0.8254 %EPT-Baetidae 0.7083 0.927 0.7623 1 0.5753 0.5846 0.7064 0.5014 # insect families 0.8671 0.6148 0.6221 0.5753 1 0.6103 0.5024 0.4675 % sh+pred 0.5635 0.6205 0.5287 0.5846 0.6103 1 0.6513 0.3199 %PT 0.6225 0.6402 0.5509 0.7064 0.5024 0.6513 1 0.3749 %tol BMIs 0.5272 0.4952 0.8254 0.5014 0.4675 0.3199 0.3749 1

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Table A9-27 Ecology Consultants, Inc. Table A-10 ANOVAs of Updated IBI, 2009 IBI, and New Core Metrics (n=273)

Parameter r-square p Group n Mean Std Error Lower 95% Upper 95% Updated IBI Scor 0.621419 <0.0001 HIGH DIST 129 13.8837 1.1411 11.637 16.13 MOD DIST 88 35.7159 1.3816 32.996 38.436 REF 56 56.0893 1.732 52.679 59.499 2009 IBI Score 0.615053 <0.0001 HIGH DIST 129 12.4574 1.1387 10.216 14.699 MOD DIST 88 33.0795 1.3786 30.365 35.794 REF 56 54.3036 1.7282 50.901 57.706 #EPT families 0.591059 <0.0001 HIGH DIST 129 3.0155 0.28101 2.462 3.569 MOD DIST 88 8.0114 0.34023 7.342 8.681 REF 56 12.7857 0.4265 11.946 13.625 % sens BMIs 0.537397 <0.0001 HIGH DIST 129 4.3883 1.2193 1.988 6.789 MOD DIST 88 20.531 1.4762 17.625 23.437 REF 56 43.2622 1.8506 39.619 46.906 TV avg. 0.549711 <0.0001 HIGH DIST 129 6.8158 0.07959 6.6591 6.9725 MOD DIST 88 5.56259 0.09636 5.3729 5.7523 REF 56 4.25709 0.12079 4.0193 4.4949 #Insect families 0.509606 <0.0001 HIGH DIST 129 10.9767 0.49344 10.005 11.948 MOD DIST 88 18.7159 0.59743 17.54 19.892 REF 56 25.4107 0.74891 23.936 26.885 %PT 0.462203 <0.0001 HIGH DIST 129 2.0178 0.518 0.998 3.038 MOD DIST 88 7.2927 0.62717 6.058 8.527 REF 56 16.3119 0.7862 14.764 17.86 %sh+pred 0.448589 <0.0001 HIGH DIST 129 5.1076 0.52491 4.074 6.141 MOD DIST 88 10.7938 0.63553 9.543 12.045 REF 56 19.135 0.79668 17.567 20.704 %tol BMIs 0.392582 <0.0001 HIGH DIST 129 67.1763 1.7307 63.769 70.584 MOD DIST 88 43.3448 2.0954 39.219 47.47 REF 56 28.404 2.6267 23.233 33.575

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Table A10-28 Ecology Consultants, Inc. Table A-11 Summary of Linear Regressions of Average Annual Rainfall vs. Physiochemical and BMI Parameters

Response Variable (y) r-square p linear fit Wet width 0.071 <0.0001 Wet width (ft) = 8.2738804 + 0.1372599*avg. rainfall (in) Habitat assessment score 0.0002 0.8117 Stream temperature 0.0004 0.2616 Dissolved oxygen 0.104 <0.0001 Dissolved oxygen (mg/l) = 7.7033944 + 0.0565639*avg. rainfall (in) Specific conductance 0.029 0.0049 Specific cond. (microS @ 25 c) = 1683.4123 - 9.5319731*avg. rainfall (in) % riparian canopy cover 0.007 0.2286 # EPT families 0.006 0.1965 % sensitive BMIs 0.039 0.0011 % sens BMIs = 25.642736 - 0.3337122*avg. rainfall (in) TV avg. 0.00002 0.938 # insect families 0.013 0.0647 % sh+pred 0.031 0.0035 % sh+pred = 12.66749 - 0.1177353*avg. rainfall (in) % PT 0.019 0.0242 % PT = 8.8565599 - 0.0911591*avg. rainfall (in) % tolerant BMIs 0.036 0.0017 % tol BMIs = 61.151727 - 0.3970874*avg. rainfall (in) BMI Density 0.036 0.0017 BMI Density #/sq. m = 1604.7397 - 19.38963*avg. rainfall (in) Baetidae 0.404 <0.0001 Baetidae = -9.882031 + 2.8473845*avg. rainfall (in) Caenidae 0.074 <0.0001 Caenidae = 14.606551 - 0.3086827*avg. rainfall (in) Leptohyphidae 0.028 0.0052 Leptohyphidae = 10.566548 - 0.1950341*avg. rainfall (in) Chironomidae 0.002 0.5102 Simulidae 0.045 0.0004 Simulidae = 7.6611737 + 0.4423074*avg. rainfall (in) Gastropoda 0.067 <0.0001 GASTROPODA = 18.045677 - 0.4174822*avg. rainfall (in) Ostracoda 0.14 <0.0001 OSTRACODA = 38.04927 - 0.9470375*avg. rainfall (in)

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Table A11-29 Ecology Consultants, Inc. Table A-12 Results of One Way ANOVA of IBI Score by Year for REF Group

REF Group n=56 p=0.0003 r2=0.55

Year Number Mean Std Error Lower 95% Upper 95% 2000 10 60.8 2.9541 54.838 66.762 2001 4 56.75 4.6709 47.324 66.176 2002 4 68.25 4.6709 58.824 77.676 2003 4 62 4.6709 52.574 71.426 2005 3 36.6667 5.3935 25.782 47.551 2006 3 62 5.3935 51.116 72.884 2007 4 62 4.6709 52.574 71.426 2008 3 55.3333 5.3935 44.449 66.218 2009 4 63 4.6709 53.574 72.426 2010 4 49.25 4.6709 39.824 58.676 2011 4 50.25 4.6709 40.824 59.676 2012 3 57.3333 5.3935 46.449 68.218 2013 3 51.3333 5.3935 40.449 62.218 2014 3 33 5.3935 22.116 43.884

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A12-30 Ecology Consultants, Inc. Table A-13 Results of One Way ANOVA of IBI Score for HIGH DIST, MOD DIST, and REF Groups for Each Year (2000 to 2014)

Year r-square p Group n Mean Std Error Lower 95% Upper 95% 2000 0.73 <0.0001 HIGH DIST 9 20.2222 3.7694 12.443 28.002 MOD DIST 8 51.375 3.9981 43.123 59.627 REF 10 60.8 3.576 53.42 68.18 2001 0.76 0.001 HIGH DIST 6 12.3333 4.8878 1.276 23.39 MOD DIST 2 31 8.4659 11.849 50.151 REF 4 56.75 5.9863 43.208 70.292 2002 0.88 <0.0001 HIGH DIST 10 12.3 3.0387 5.889 18.711 MOD DIST 6 53.8333 3.9229 45.557 62.11 REF 4 68.25 4.8045 58.113 78.387 2003 0.82 <0.0001 HIGH DIST 11 12.6364 3.2214 5.84 19.433 MOD DIST 5 47 4.7781 36.919 57.081 REF 4 62 5.342 50.729 73.271 2005 0.64 0.0003 HIGH DIST 10 13.2 2.3967 8.119 18.281 MOD DIST 6 27.8333 3.0942 21.274 34.393 REF 3 36.6667 4.3758 27.39 45.943 2006 0.7 <0.0001 HIGH DIST 10 16.6 3.6104 9.015 24.185 MOD DIST 8 39.625 4.0365 31.145 48.105 REF 3 62 6.5916 48.152 75.848 2007 0.76 <0.0001 HIGH DIST 12 12.75 3.2731 5.943 19.557 MOD DIST 8 39.25 4.0087 30.913 47.587 REF 4 62 5.6692 50.21 73.79 2008 0.6 <0.0001 HIGH DIST 12 14 3.7453 6.187 21.813 MOD DIST 8 35.375 4.587 25.807 44.943 REF 3 55.3333 7.4906 39.708 70.958 2009 0.86 <0.0001 HIGH DIST 13 10.0769 2.2972 5.3 14.854 MOD DIST 7 30.4286 3.1305 23.918 36.939 REF 4 63 4.1413 54.388 71.612 2010 0.56 <0.0001 HIGH DIST 13 10.6154 3.639 3.069 18.162 MOD DIST 8 26.25 4.6388 16.63 35.87 REF 4 49.25 6.5603 35.645 62.855 2011 0.73 0.0002 HIGH DIST 7 16 3.5263 8.382 23.618 MOD DIST 5 26.2 4.1723 17.186 35.214 REF 4 50.25 4.6648 40.172 60.328 2012 0.44 0.0418 HIGH DIST 5 22 7.4207 5.667 38.333 MOD DIST 6 38 6.7741 23.09 52.91 REF 3 57.3333 9.5801 36.248 78.419 2013 0.41 0.0406 HIGH DIST 6 18.6667 6.5078 4.487 32.846 MOD DIST 6 27.3333 6.5078 13.154 41.513 REF 3 51.3333 9.2035 31.281 71.386 2014 0.49 0.0337 HIGH DIST 5 10.2 4.5051 0.162 20.238 MOD DIST 5 17 4.5051 6.962 27.038 REF 3 33 5.8161 20.041 45.959

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Table A13-31 Ecology Consultants, Inc. Table A-14: Burned vs. Unburned Stream Study Reaches

Study reaches in burned watersheds were compared to those in unburned watersheds for the year before (year 0) and years 1 – 5 after fires. Cumulative rainfall amounts are only shown for those sites and years when BMI samples were taken. Blanks in the Years 0 through 5 columns indicate years when no data were taken from specific sites. Two study reaches were used as both burned and unburned sites for analysis of different fires. AH1 and GAV1 were used as burned sites for the first five years (2005-2009) after the Gaviota Fire, and unburned sites for years 1-5 after the Tea and Gap (2009-2013) and Jesusita Fires (2010- 2014). Some sites were burned by both the Tea and Jesusita Fires, but these sites were sampled before the Jesusita Fire occurred. Years 0 and 1 from these sites for the Tea Fire were taken from 2008 and 2009, but if their watersheds burned to a greater extent in the Jesusita Fire, then data from pre-fire and post-fire years for the Jesusita Fire were taken from 2009 and 2010-2014, with no additional use of post- fire data from these sites for the Tea Fire. Because the Disturbance Category designations for GAV1, MONT2, SJ2, and SY2 changed over years, disturbance group designations for these sites from the pre-fire year were used.

Fire Site Fire Burned/ Dist Gradient Fire Dist from Rain (in) Year Unburned group extent fire(ft) Year 0 Year 1 Year 2 Year 3 Year 4 Year5 Gaviota AH1 2004 B REF 0.04 0.15 0 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota GAV1 2004 B MOD 0.01 0.11 0 29.3 53.2 8.6 27.9 14.9 Gaviota AB1 2004 U HIGH 0.01 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota AB2 2004 U HIGH 0.01 29.3 53.2 Gaviota AB3 2004 U MOD 0.03 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota AT1 2004 U HIGH 0 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota AT2 2004 U HIGH 0.01 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota C1 2004 U HIGH 0.01 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota C3 2004 U REF 0.03 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota M1 2004 U HIGH 0.01 29.3 53.2 28.3 8.6 27.9 Gaviota M3 2004 U MOD 0.07 29.3 53.2 28.3 8.6 27.9 Gaviota MONT1 2004 U MOD 0.05 29.3 53.2 Gaviota SA2 2004 U MOD 0.05 29.3 53.2 28.3 8.6 27.9 14.9 Gaviota SJ1 2004 U HIGH 0.01 29.3 53.2 28.3 Gaviota SJ2 2004 U HIGH 0.01 29.3 53.2 28.3 8.6 27.9 Gaviota SJ3 2004 U REF 0.11 29.3 53.2 28.3 8.6 14.9 Gaviota SY1 2004 U HIGH 0.01 29.3 53.2 28.3 8.6 27.9 Gaviota SY2 2004 U HIGH 0.03 29.3 53.2 28.3 8.6 27.9 Tea M1 2008 B HIGH 0.01 0.03 25935 27.9 14.9 30 36.3 15.1 13.1 Tea M3 2008 B MOD 0.07 0.04 7218 27.9 14.9 30 36.3 15.1 13.1 Tea M4 2008 B REF 0.08 0.11 0 27.9 14.9 30 36.3 15.1 13.1 Tea MONT2 2008 B MOD 0.03 0.02 10827 27.9 14.9 30 Gap SJ2 2008 B HIGH 0.01 0.28 4921 27.9 14.9 30 36.3 15.1 13.1 Tea SY1 2008 B HIGH 0.01 0.67 3445 27.9 14.9 30 36.3 15.1 13.1 Tea SY2 2008 B MOD 0.03 0.86 1148 27.9 14.9 30 36.3 15.1 13.1 Gap T3 2008 B HIGH 0.01 0.3 8399 27.9 14.9 30 Tea/Gap AB1 2008 U HIGH 0.01 27.9 14.9 Tea/Gap AB3 2008 U MOD 0.03 27.9 14.9 Tea/Gap AH1 2008 U REF 0.04 27.9 14.9 30 36.3 15.1 13.1 Tea/Gap AT1 2008 U HIGH 0 27.9 14.9 Tea/Gap AT2 2008 U HIGH 0.01 27.9 14.9 Tea/Gap C1 2008 U HIGH 0.01 27.9 14.9 30 36.3 15.1 13.1 Tea/Gap C3 2008 U REF 0.03 27.9 14.9 30 36.3 15.1 13.1 Tea/Gap GAV1 2008 U MOD 0.01 27.9 14.9 30 36.3 15.1 13.1 Tea/Gap RIN1 2008 U MOD 0.02 27.9 14.9 30 Tea/Gap SA2 2008 U MOD 0.05 27.9 14.9 Jesusita AB1 2009 B HIGH 0.01 0.5 19472 14.9 30 36.3 15.1 13.1 10 Jesusita AB3 2009 B MOD 0.03 0.75 246 14.9 30 36.3 15.1 13.1 10 Jesusita AT1 2009 B HIGH 0 0.2 23615 14.9 30 Jesusita AT2 2009 B HIGH 0.01 0.24 15846 14.9 30 Jesusita M1 2009 B HIGH 0.01 0.45 22654 14.9 30 36.3 15.1 13.1 10 Jesusita M3 2009 B MOD 0.07 0.69 3937 14.9 30 36.3 15.1 13.1 10 Jesusita M4 2009 B REF 0.08 0.67 427 14.9 30 36.3 15.1 13.1 10 Jesusita MONT2 2009 B MOD 0.03 0.1 14436 14.9 30 Jesusita SA2 2009 B MOD 0.05 0.49 230 14.9 30 13 Jesusita AH1 2009 U REF 0.04 14.9 30 36.3 15.1 13.1 10 Jesusita C1 2009 U HIGH 0.01 14.9 30 36.3 15.1 13.1 10 Jesusita C3 2009 U REF 0.03 14.9 30 36.3 15.1 13.1 10 Jesusita GAV1 2009 U MOD 0.01 14.9 30 36.3 15.1 13.1 10 Jesusita RIN0 2009 U MOD 0.01 14.9 30 Jesusita RIN1 2009 U MOD 0.02 14.9 30 Jesusita SJ3 2009 U REF 0.11 14.9 30

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A14-32 Ecology Consultants, Inc. Table A-15: Results of ANOVAs of Fire and Disturbance Effects on Stream Response Variables

Results of two-way ANOVA testing the effects of human disturbance category (REF, MOD DIST, HIGH DIST) and wildfire (Burned vs. Unburned), and their interaction, on riparian canopy cover (%), stream temperature (oC), habitat assessment score, and IBI score for the year before (year 0) and for five years after (years 1 to 5) fires. The degrees of freedom for each analysis in each year are shown in parentheses, with F and p values for the overall ANOVA and significant factors (human disturbance = D, fire = F), or their interaction, shown with asterisks denoting the level of statistical significance (* = p < 0.05, ** p < 0.01, *** = p < 0.001, **** = p < 0.0001) in the body of the table.

Response Year 0 Year 1 Year 2 Year 3 Year 4 Year 5 variable (5,46) (5, 46) (5, 31) (5, 28) (5, 28) (5, 23) Canopy 4.2, 0.003 2.4, 0.048 3.5, 0.012 3.3, 0.02 2.3, 0.08 1.7, >0.10 cover D** D* D** D* D* Temperatur 2.2, 0.07 2.7, 0.03 4.0, 0.006 2.1, 0.09 5.0, 0.002 2.8, 0.04 e D** D** D** D* D*** D*, F* 38.4, < Habitat 26, <0.0001 18, <0.0001 21, <0.0001 16, <0.0001 20, <0.0001 0.0001 score D**** D****, F* D**** D**** D**** D**** 18, < 22, <0.0001 12, <0.0001 24, <0.0001 13, <0.0001 7.6, 0.0003 0.0001 IBI score D****, D**** D****, F* D****, F** D**** D**** FXD*

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Table A15-33 Ecology Consultants, Inc. Table A-16: Multiple Regression Analyses Results of Fire Effects on Stream Response Variables

Results of multiple regression analysis where riparian canopy cover, stream temperature, habitat assessment score, and IBI score were treated as response variables and gradient, cumulative rainfall (in.), fire extent (% of drainage basin burned), and downstream distance from the fire (ft), were entered as independent variables for years 1 through 5 after fires. Numbers in parentheses after years are degrees of freedom for tests. Analysis were only done on sites affected by fire. The direction and magnitude of significant regression coefficients (* = < 0.05, ** = <0.01, *** = <0.001, **** = < 0.0001) and overall F and p values are shown.

Distance Overall F and p Variable Gradient Rain Fire extent from fire values Year 1 (4,14) Canopy cover -1.1* 2.7, 0.07 Temperature +8.1** +0.0002* 6.2, 0.004 Habitat score +958*** +0.78* 12.8, 0.0001 IBI score +278* -28** -0.0008* 9.4, 0.0007 Year 2 (4,9) Canopy cover 1.2, 0.39 Temperature +0.0003* 4.2, 0.03 Habitat score 6.0, 0.012 IBI score 2.0, 0.17 Year 3 (4,8) Canopy cover 1.8, 0.22 Temperature +0.0002* 3.8, 0.05 Habitat score +670**** -1.0*** -20* -0.0013*** 60, <0.0001 IBI score +193* -0.53** -0.0014*** 30, <0.0001 Year 4 (4,9) Canopy cover 3.3, 0.06 Temperature +0.0002* 7.9, 0.005 Habitat score +715*** +2.1* 19.9, 0.0002 IBI score 6.7, 0.008 Year 5 (4,8) Canopy cover +520* 4.0, 0.05 Temperature 4.4, 0.04 Habitat score 8.8, 0.005 IBI score 5.9, 0.016

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A16-34 Ecology Consultants, Inc. Table A-17 ANOVAs of Individual BMI Taxa Abundances in Estuaries for REF, MOD DIST,and HIGH DIST Groups

Taxa Prelim DIST To r-square p DIST Group n Mean Std Error Lower 95% Upper 95% Baetidae Sensitive 0.179922 0.0759 HIGH DIST 14 4.7143 7.847 -11.42 20.844 MOD DIST 7 23.8571 11.097 1.05 46.668 REF 8 34.625 10.381 13.29 55.963 Aeshnidae Sensitive 0.113858 0.2078 HIGH DIST 14 0.071429 0.24823 -0.4388 0.5817 MOD DIST 7 0 0.35105 -0.7216 0.7216 REF 8 0.75 0.32837 0.075 1.425 Acari Sensitive 0.21464 0.0432 HIGH DIST 14 0.07143 0.21198 -0.3643 0.5072 MOD DIST 7 0.28571 0.29979 -0.3305 0.9019 REF 8 1 0.28043 0.4236 1.5764 Amphipoda Sensitive 0.30605 0.0087 HIGH DIST 14 1.7143 4.3376 -7.2 10.63 MOD DIST 7 1.5714 6.1343 -11.04 14.181 REF 8 24.5 5.7381 12.71 36.295 Mystidacea Sensitive 0.273865 0.0156 HIGH DIST 14 0 0.51355 -1.056 1.0556 MOD DIST 7 0 0.72627 -1.493 1.4929 REF 8 2.5 0.67937 1.104 3.8965 Isopoda Sensitive 0.340029 0.0045 HIGH DIST 14 3.3571 4.4537 -5.8 12.512 MOD DIST 7 3.1429 6.2984 -9.8 16.089 REF 8 28.625 5.8916 16.51 40.735 Polychaeta Sensitive 0.123291 0.1808 HIGH DIST 14 1.64286 1.3649 -1.163 4.4484 MOD DIST 7 0 1.9302 -3.968 3.9676 REF 8 4.875 1.8056 1.164 8.5864 Chironomidae Moderate 0.263509 0.0188 HIGH DIST 14 16.1429 6.5022 2.777 29.508 MOD DIST 7 49.4286 9.1955 30.527 68.33 REF 8 19.625 8.6016 1.944 37.306 Coenagrionidae Moderate 0.176045 0.0807 HIGH DIST 14 0.071429 0.20069 -0.3411 0.484 MOD DIST 7 0.857143 0.28382 0.2737 1.4405 REF 8 0.125 0.26549 -0.4207 0.6707 Libeluliidae Moderate 0.157385 0.1079 HIGH DIST 14 0.285714 0.1681 -0.0598 0.6312 MOD DIST 7 0.714286 0.23773 0.2256 1.2029 REF 8 0 0.22237 -0.4571 0.4571 Gastropoda Moderate 0.052488 0.4961 HIGH DIST 14 5.35714 2.8543 -0.51 11.224 MOD DIST 7 0.71429 4.0366 -7.583 9.012 REF 8 7.125 3.7759 -0.636 14.886 Copepoda Moderate 0.012141 0.8532 HIGH DIST 14 0.78571 0.51608 -0.2751 1.8465 MOD DIST 7 0.57143 0.72984 -0.9288 2.0716 REF 8 1.125 0.68271 -0.2783 2.5283 Dytisidae Tolerant 0.084821 0.3159 HIGH DIST 14 1.64286 0.57609 0.459 2.827 MOD DIST 7 0.42857 0.81471 -1.246 2.1032 REF 8 0.375 0.76209 -1.192 1.9415 Corixidae Tolerant 0.210464 0.0463 HIGH DIST 14 55.2143 11.098 32.4 78.026 MOD DIST 7 22.2857 15.695 -9.98 54.547 REF 8 9.75 14.681 -20.43 39.927 Ostracoda Tolerant 0.256299 0.0213 HIGH DIST 14 52.7143 8.017 36.23 69.194 MOD DIST 7 12 11.338 -11.31 35.306 REF 8 31.625 10.606 9.82 53.426 Cladocera Tolerant 0.033619 0.6411 HIGH DIST 14 11.2143 5.6059 -0.31 22.737 MOD DIST 7 10.1429 7.9279 -6.15 26.439 REF 8 2.625 7.4159 -12.62 17.869 Oligochaeta Tolerant 0.118421 0.1943 HIGH DIST 14 5.0714 3.0054 -1.106 11.249 MOD DIST 7 11 4.2503 2.263 19.737 REF 8 0.125 3.9758 -8.047 8.297 note: mean abundance of 0.5 for at least one of the disturbance groups required for consideration

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A17-35 Ecology Consultants, Inc. Table A-18 ANOVAs of Estuary BMI Metrics for REF, MOD DIST,and HIGH DIST Groups

Metric r-square p DIST Group n Mean Std Error Lower 95% Upper 95% % Sensitive BMIs 0.742353 <0.0001 HIGH DIST 14 7.5714 3.6634 0.041 15.102 MOD DIST 7 15.7619 5.1808 5.113 26.411 REF 8 59.0417 4.8462 49.08 69.003 % Tolerant BMIs 0.706528 <0.0001 HIGH DIST 14 77.0952 4.0797 68.709 85.481 MOD DIST 7 43.4959 5.7695 31.636 55.355 REF 8 25.7917 5.3969 14.698 36.885 BMI Density 0.117089 0.1981 HIGH DIST 14 3172.5 565.96 2009 4335.8 MOD DIST 7 1431.31 800.39 -214 3076.5 REF 8 2115.81 748.69 577 3654.8 # Taxa 0.030665 0.6671 HIGH DIST 14 8.07143 0.61269 6.812 9.331 MOD DIST 7 7.42857 0.86648 5.6475 9.21 REF 8 8.5 0.81052 6.834 10.166 # Sensitive Taxa 0.314625 0.0074 HIGH DIST 14 2.28571 0.28511 1.6997 2.8718 MOD DIST 7 1.85714 0.40321 1.0283 2.686 REF 8 3.625 0.37717 2.8497 4.4003 # Tolerant Taxa 0.246811 0.0251 HIGH DIST 14 3.5 0.2407 3.0052 3.9948 MOD DIST 7 2.42857 0.3404 1.7289 3.1283 REF 8 2.625 0.31842 1.9705 3.2795 #Sens/Tol taxa 0.366612 0.0026 HIGH DIST 14 0.65 0.18766 0.2643 1.0357 MOD DIST 7 0.7381 0.2654 0.1926 1.2836 REF 8 1.80833 0.24826 1.298 2.3186 % Insects 0.196197 0.0585 HIGH DIST 14 48.3333 7.15 33.636 63.031 MOD DIST 7 69.7981 10.112 49.013 90.584 REF 8 35.1667 9.459 15.724 54.61 % non-insects 0.204452 0.0511 HIGH DIST 14 51.4762 7.08 36.924 66.029 MOD DIST 7 30.2971 10.012 9.717 50.878 REF 8 65.5833 9.366 46.332 84.835 % Dominant Taxo 0.122284 0.1835 HIGH DIST 14 55.1429 3.6962 47.545 62.741 MOD DIST 7 43.4359 5.2273 32.691 54.181 REF 8 48.2083 4.8897 38.158 58.259 % 2 Dominant Tax 0.089579 0.2952 HIGH DIST 14 77.5952 3.2054 71.006 84.184 MOD DIST 7 71.0928 4.5331 61.775 80.411 REF 8 70 4.2403 61.284 78.716 % Predators 0.245818 0.0255 HIGH DIST 14 34.2857 5.9741 22.01 46.566 MOD DIST 7 19.3249 8.4487 1.96 36.691 REF 8 5.8333 7.903 -10.41 22.078 % Collector-gathe 0.303655 0.0091 HIGH DIST 14 61.9048 5.4762 50.648 73.16 MOD DIST 7 78.5541 7.7446 62.635 94.47 REF 8 91.9167 7.2444 77.026 106.81

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A18-36 Ecology Consultants, Inc. Table A-19 ANOVAs of % Sensitive BMIs and % Tolerant BMIs for REF, MOD DIST,and HIGH DIST Groups by Year, 2012- 2014 Year Metric r-square p DIST Group n Mean Std Error Lower 95% Upper 95% 2012 % sens BMIs 0.91 <0.0001 HIGH DIST 6 7.2222 4.2883 -2.48 16.923 MOD DIST 2 7.6667 7.4276 -9.14 24.469 REF 4 68.333 5.2521 56.45 80.214 % tol BMIs 0.8 0.0008 HIGH DIST 6 76.111 6.043 62.44 89.782 MOD DIST 2 49 10.467 25.321 72.679 REF 4 19.333 7.401 2.59 36.077 2013 % sens BMIs 0.8 0.0083 HIGH DIST 5 9.3333 5.5993 -4.37 23.034 MOD DIST 2 31.833 8.8532 10.17 53.496 REF 2 59.5 8.8532 37.84 81.163 % tol BMIs 0.78 0.0104 HIGH DIST 5 79.333 7.987 59.79 98.876 MOD DIST 2 33 12.628 2.1 63.9 REF 2 16.833 12.628 -14.07 47.733 2014 % sens BMIs 0.59 0.1098 HIGH DIST 3 5.3333 8.628 -16.85 27.513 MOD DIST 3 10.444 8.628 -11.74 32.624 REF 2 40 10.568 12.84 67.165 % tol BMIs 0.74 0.0358 HIGH DIST 3 75.333 5.9661 59.997 90.67 MOD DIST 3 46.824 5.9661 31.487 62.16 REF 2 47.667 7.3069 28.884 66.45

Southern Coastal Santa Barbara Streams and Estuaries Bioassessment Program 2014 Report and Updated Index of Biological Integrity Page A19-37 Ecology Consultants, Inc.

APPENDIX B:

ESTUARY HABITAT ASSESSMENT SCORING SHEET

SANTA BARBARA ESTUARY HABITAT ASSESSMENT

Date: Time: Crew: Estuary: Site ID:

Condition Category Habitat Reference Moderately Disturbed Highly Disturbed Component 1., 2. Estuary Less than 20% of historical 20-50% of historical estuary Greater than 50% of historical Form and estuary form (i.e. surface area) form and/or perimeter estuary form and/or perimeter Perimeter and/or perimeter altered or altered or infringed on. altered or infringed on. infringed on. Alterations may include fill, berms, riprap, wing walls, and development (homes, parking lots, parks, agriculture, etc.). Score 20 15 10 5 0 3. Estuary Estuary has a variety of habitats Open water habitat and/or Open water habitat and/or Habitat including open water, fringing fringe wetlands have been fringe wetlands have been Diversity salt marsh, tidal creeks, salt flats, moderately reduced (20- greatly reduced (>50%) due to and/or freshwater marsh. Fringe 50%) due to development, development, filling, or wetlands have not been largely filling, or dredging. dredging. reduced (>20%) due to development, filling, or dredging. Score 10 7.5 5 2.5 0 4. Estuary Estuary habitat not fragmented, Moderate fragmentation Major fragmentation of estuary Habitat and is freely connected with between aquatic habitats habitat and/or between estuary Connectivity adjoining stream, ocean, and (i.e., 1 or 2 small grade and adjoining stream, ocean, wetland habitats. No major drops or berms) that and/or wetlands. Major movement barriers or partially restricts movement restrictions to movement of impediments (e.g., grade of species between wetland aquatic species. changes at road or railroad habitats, but no complete crossings, artificial berms or barriers to movement. levees) to aquatic species. Score 10 7.5 5 2.5 0 5. Hydrology Estuary with natural freshwater Moderate freshwater Major freshwater diversions inputs from upstream (little or no diversion upstream (e.g., (e.g., dams, heavy groundwater

diversions), flows between small reservoir, groundwater use) and/or artificial freshwater estuary and ocean allowed to pumping), or moderate inputs (e.g., intensive ag/urb exist naturally. No manipulation added freshwater inputs return flows, sewage treatment of beach berm between estuary (i.e., from ag/urb runoff). plant). Beach berm between and ocean (if it develops). Occasional breaching of estuary and ocean routinely beach berm, but not routine breached throughout dry or ongoing throughout the season. dry season. Score 10 7.5 5 2.5 0 6. Substrate Substrate natural sand, fines, Moderate disturbances to Major disturbances to sediment and/or coarse sediments. No or sediment (i.e., foot traffic, (dredging, extreme trampling)

minor artificial removals (e.g., past dredging) or moderate or major increases in fine dredging) or additions increased sedimentation sediment deposition from (sedimentation). 0-25% of (i.e., stream or bank stream or eroding banks that estuary bottom sediments erosion) from upstream affect >50% of the estuary impacted. development that affect 25- bottom. 50% of estuary bottom. Score 10 7.5 5 2.5 0

SANTA BARBARA ESTUARY HABITAT ASSESSMENT

Condition Category Habitat Reference Moderately Disturbed Highly Disturbed Component 7. Water Column Maximum water depth 4’ or Maximum water depth 2-4’, Maximum water depth under 2’ greater, no or only minor visible moderate visible water high level of trash, animal

water pollution (trash, animal pollution, daytime dissolved waste, or other visible water waste, oily sheens). Daytime oxygen levels not optimal, pollution present. Daytime dissolved oxygen levels optimal but >5 mg/l and <15 mg/l. dissolved oxygen levels <5 mg/l and presumed to be stable (6-12 or >15 mg/l (night DO crash mg/l). likely with shallow depth, high algae levels. Score 10 7.5 5 2.5 0 8. Aquatic Mix of submerged (e.g. eelgrass, Submerged/emergent native No native submerged or Vegetation pond weeds, algae) and/or vegetation present but emergent vegetation present, or emergent (e.g. pickleweed, reduced. Some seaweed only algae present. Seaweed bulrush, cattail, rushes) mostly rack present. rack sparse, missing, or largely native vegetation and seaweed replaced with ornamental rack present. No vegetation terrestrial plant litter. removals. Score 10 7.5 5 2.5 0 9. Riparian/ Estuary buffered by natural Natural buffer habitat Natural buffer habitat is less Upland riparian/upland habitat of 25 reduced to 10-25 meters in than 10 meters in average Buffer meters or greater in average average width. Natural width around estuary. Natural width. Vegetation is allowed to vegetation has been subject vegetation has been largely grow naturally, and at least 80% to partial clearing and/or cleared and replaced by non- of vegetative cover is native. moderate invasion by non- native plant species. Less than Impacts to buffer habitat are native plant species. 50- 50% of vegetation is native. minor (e.g. walking trails), no 80% of vegetation is native. other clearing of vegetation or other alterations. Score 10 7.5 5 2.5 0 10. Foot Traffic, Buffer habitat largely shields Moderate level of impacts High level of impacts due to Noise, estuary from impacts associated occur due to moderate tightly adjoining high intensity Lighting with human and pet foot traffic, intensity of nearby development (e.g. major noise, lighting, air emissions, etc. development and easy highway, industrial plant, dense Light impacts of this nature may access to a portion of the urban uses, intensive ag./rec. occur (e.g., hikers, light beach estuary, which may be uses, etc.). Most of estuary traffic, nearby campers or roads, located next to a popular fringe is easily accessed and homes, etc.). Most of estuary is beach, campground, or directly impacted by vehicles, protected or not easily accessed. housing development. livestock, and human/pet foot traffic. Score 10 7.5 5 2.5 0 Total Score /100