Reduction of Runoff Pollutants from Major Arterial Roads Using Porous Pavement

Abstract

Stormwater runoff from large roads is a major source of pollutants to receiving waters, and reduction of these pollutants is important for sustainable water resources and transportation networks. Porous pavements have been shown to substantially reduce many of these pollutants, but studies are lacking on arterial roads. We sampled typical stormwater pollutants in runoff from sections of an arterial road 9–16 years after installation of three pavement types: control with conventional asphalt, porous asphalt overly, and full-depth porous asphalt. Both types of porous pavements substantially reduced most of the stormwater pollutants measured. Total suspended solids, turbidity, total lead, total copper, and 6PPD-quinone were all reduced by >75%. Total nitrogen, ammonia, total phosphorus, biochemical oxygen demand, total and dissolved copper, total mercury, total zinc, total polycyclic aromatic hydrocarbons, and di-2-ethylhexyl phthalate were all reduced by >50%. Reductions were lower or absent for nitrate, orthophosphate, E. coli, dissolved lead, and dissolved zinc. Most reductions were statistically significant. Many pollutants exceeded applicable water quality standards in the control samples but met them with both types of porous pavement. This study demonstrates that porous overlays and full-depth porous asphalt can provide substantial reductions of several priority stormwater pollutants on arterial roads for many years after installation. Porous pavements have the potential to substantially enhance water quality of urban waterways and provide ecological benefits on urban thoroughfares.

1. Introduction

Urbanization has steadily increased since 1950; more than 50% of the global population currently lives in urban areas compared to 33% in the 1950s and is expected to increase to 66% by 2050 [1]. Urbanization is more pronounced in industrialized countries, where it is expected that 86% of the population will live in urban areas compared to 64% of the population in developing countries by 2050 [2]. In the United States, 81% of the population lives in urban areas [3]. Other regions have much higher rates of urbanization, such as the Gulf Cooperation Council countries (United Arab Emirates, Bahrain, Kuwait, Oman, Qatar, and Saudi Arabia), where 82% of the population currently lives in urban areas [4]. Urbanization has caused environmental degradation, pollution from stormwater and wastewater, and air pollution [2]. Impervious areas increase as a result of urban development, including roads, parking lots, and buildings. Stormwater from roads contains contaminants from cars and pollutants deposited on the roadway, which is then transported to receiving waters [5,6]. These pollutants negatively impact aquatic organisms and biogeochemical cycles [5,6,7]. Many common roadway pollutants, such as copper, zinc, tire chemicals, and hydrocarbons, have been shown to be toxic to aquatic species, particularly salmon, at concentrations observed in stormwater [8,9,10,11,12]. Stormwater treatment is needed to protect water sources as a sustainable natural resource.

Common stormwater treatment techniques such as vegetated green infrastructure and porous pavements can reduce contaminants discharging to aquatic ecosystems, reduce flooding and erosion, and reconnect the hydrologic cycle. Many cities have implemented green stormwater infrastructure to slow and treat runoff [13,14,15]. “Sponge cities” rely on vegetated green infrastructure and permeable surfaces to increase infiltration and manage flooding [16]. Vegetated green stormwater infrastructure typically consists of an inlet draining runoff from the street or building to a land area with soil and plants. These systems have been shown to be effective at removing stormwater contaminants [17,18,19,20,21,22]. In many highly urbanized and industrial areas, space is limited or nonexistent for vegetated green infrastructure. These areas typically have high pollutant loads and could benefit from an alternative treatment method. Porous pavement may be one way to effectively treat stormwater in these areas without additional space requirements.

Porous pavements are made by reducing the sand and fines content used in conventional pavement mixes, which results in a pavement with small, interconnected pore spaces that allow stormwater to move through the pavement and drain to the base aggregate and soil below the pavement [23]. Porous overlays, also called pervious friction courses, are also used, which include a layer of porous asphalt (typically 25–76 mm or 1–3 in thick) on top of conventional impervious pavement. Porous overlays allow for drainage of stormwater below the overlay to a stormwater inlet, providing many of the same benefits as full-depth porous pavements but without infiltration. Porous pavements can reduce the urban heat island effect and increase road safety. Porous pavements have been designated “cool pavements” by the U.S. Environmental Protection Agency (EPA), which are defined as paving materials that reflect more solar energy and retain more water than conventional pavement [24,25]. Road safety is also improved by significantly reducing standing water on streets, which reduces hydroplaning and improves skid resistance [26,27]. Reductions in tire noise and water spray, as well as improved nighttime visibility, have also been observed [24], and the rough texture of porous pavements provides more traction for vehicles. The Texas Department of Transportation evaluated porous asphalt sections from 2003 to 2011 and found that porous asphalt lowers noise levels, increases skid resistance, reduces the number of accidents, injuries, and fatalities, and requires little to no maintenance compared to conventional pavement [28]. They also observed minimal raveling and delamination. Because porous pavements effectively drain stormwater, there is less maintenance required for fixing potholes and cracking compared to conventional pavement [23]. The main concern with porous pavements is clogging of the pore spaces, which can be minimized by vacuum sweeping on an annual to monthly basis, depending on sediment load. In addition to lower maintenance costs, the overall cost of porous pavements can be lower due to the elimination of drainage systems and piping for stormwater conveyance [29].

Studies have shown that pollutant removal with porous pavements is generally as effective as bioretention and other types of vegetated green infrastructure [30,31,32,33,34,35,36,37]. Several studies have shown a significant reduction in total suspended solids (TSS), with many observing >90% removal [31,35,36,38,39,40]. Many studies have observed significant removal of metals [31,32,34]. On average, the removal of total copper, zinc, and lead is ~67% in porous pavements [35,38,39,41,42,43,44]. Physical removal as the stormwater drains through the pore spaces of the pavement is likely the main removal mechanism of metals and TSS [45], with the majority of lead, zinc, copper, and cadmium removed in the top 30 cm (~12 in) of the pavement [46,47]. Higher removal was observed for contaminants that tend to attach to particles [38,44]. Studies on porous overlays have shown similar TSS and metals removal [48]. Removal of hydrocarbons and polycyclic aromatic hydrocarbons (PAHs) has also been significant [30,31,34,36]. Many studies reported the removal of hydrocarbons to levels below detection limits [30,34,36]. Results for nutrients have been mixed; some studies have found 80–96% removal of nitrogen and phosphorus [33,49], whereas other studies found no removal or leaching of nitrogen and phosphorus [39,50,51]. More studies on nutrients are needed to determine the mechanisms of nitrogen and phosphorus removal and to optimize removal in porous pavements. In the few studies evaluating E. coli, >90% removal was observed [52,53]. Although results are promising, most studies on porous pavements have either taken place in the laboratory [40,43,44,49] or focused on parking lots [31,35,36,37], highways [38,39,41], and residential areas [40,42]. To our knowledge, there are no studies on water quality of porous pavements for arterial roads. Arterial roads are unique in that they experience high traffic volumes traveling at moderate speeds compared to slower residential roads and high-speed highways and are generally swept more frequently. Due to their traffic loads, runoff from arterial roads can be a primary source of pollutants in urban streams. More field studies on arterial roads are needed to fully understand the benefits of porous pavements.

Despite the safety and water quality benefits of porous pavements, there is still a reluctance by some transportation agencies to implement porous pavements on a large scale. Additional field studies are needed to provide data to evaluate performance over time and aid in developing design guidelines. This study evaluates an arterial road with a section of 7.6 cm (3 in) porous asphalt overlay and a section of 20.3 cm (8 in) full-depth porous asphalt installed in 2008 in comparison with a section of conventional asphalt. All of these sections drain to an existing stormwater system. Grab samples were taken during multiple storm events and analyzed for metals, nutrients, TSS, hydrocarbons, E. coli, and the tire chemical N-(1,3-dimethylbutyl)-N’-phenyl-p-phenylenediamine-quinone (6PPD-quinone). We hypothesize that significant removal of contaminants will occur in the porous pavement and porous overlay compared to the conventional pavement.

2. Materials and Methods

2.1. Sampling Sites

All sites were on Kane Drive in Gresham, Oregon, U.S.A. (Figure 1). Annual precipitation in Gresham is 112 cm (44 in), with most precipitation occurring during the rainy months (Nov–Mar) and little to no precipitation occurring July–October [54]. Kane Drive is a five-lane arterial road with >30,000 vehicle trips per day and is a truck route for freight transport from Interstate 84 to Highway 26. Kane Drive is representative of high-traffic arterial roads that convey large numbers of vehicles through urban areas and, therefore, produce relatively high levels of pollutants. Stormwater runoff generally drains from Kane Drive to Kelly Creek, a tributary to the salmon-bearing Beaver Creek and Sandy River. A 292 m (958 ft) section of 20.3 cm (8 in) porous asphalt and a 532 m (1745 ft) section of a 7.6 cm (3 in) porous asphalt overlay over 12.7 cm (5 in) of conventional asphalt were installed in 2008. Because full infiltration was not feasible due to low infiltrating soils, runoff from both sections drains to an existing stormwater system. A sweep of the curb lanes is conducted monthly with a vacuum street sweeper and additional sweeps as needed for leaf fall or cleanup of winter weather traction applications.

Three sampling sites were chosen to compare the porous asphalt overlay and the full-depth porous asphalt to conventional asphalt (Figure 1). The conventional asphalt site was the control and is approximately 1200 m (~4000 ft) from the other two sites. The stormwater system was accessed from either a manhole or catch basin that receives runoff from each of the three pavement types. Sites were selected at locations that received drainage from each type of pavement and have similar drainage areas (0.50–0.63 ha or 1.25–1.55 acres).

2.2. Sample Collection

Five storms were sampled from 2017 to 2024, when the road had been in place for 9–16 years. Storms ranged in size from 1.0 to 4.0 cm (0.41 to 1.59 in) over 24 h, and all were preceded by an antecedent dry period of at least 12 h. Grab samples were collected at each site in three rounds during the storms, targeting the rising limb, peak, and falling limb of the hydrograph. Rounds of grab samples were collected at least one hour apart, and samples among sites within a round were collected within one hour. Grab samples were collected by removing the lid of the manhole or catch basin and collecting runoff flowing through the pipe with a stainless steel bailer on a telescoping rod. Field measurements were collected, and sample water was immediately placed into the appropriate sample bottles and delivered to a laboratory for analysis in coolers on ice.

2.3. Water Quality Analysis

Turbidity, pH, conductivity, and temperature were measured at the site when grab samples were collected. Samples were analyzed for TSS, nutrients, biochemical oxygen demand (BOD), metals, E. coli, PAHs, and phthalates at the City of Portland Water Pollution Control Lab.

Table 1. Analysis methods for each water quality analyte.

Analyte	Method
Turbidity	Hach 2100Q Turbidimeter (Hach Company: Loveland, CO, USA)
pH, conductivity, temperature, dissolved oxygen	YSI Pro Plus Multi-Meter Probe (YSI: Yellow Springs, OH, USA)
Ammonia, nitrate	EPA 300.0
Phosphate	EPA 365.1
Total Kjeldahl Nitrogen (TKN)	EPA 351.2
Total Phosphorus	EPA 365.4
5-Day Biochemical Oxygen Demand (BOD)	SM 5210B
Total Suspended Solids (TSS)	SM 2540D
Total mercury, lead, copper, zinc	EPA 200.8
Dissolved lead, copper, zinc	EPA 200.8
E. coli	SM 9223B
PAHs and phthalates	EPA 8270-SIM
6PPD-quinone	ALS Environmental Laboratories In-House Method

lists the methods for each analyte. Standard methods were followed for sample bottle preparation and sample preservation [55]. The emerging pollutant 6PPD-quinone was added to sampling in 2021 [10] and collected in high-density polyethylene (HDPE) bottles during three storms. ALS Environmental Laboratories used LC/MS–MS with a solid phase extraction to quantify 6PPD-quinone. There was no standard or EPA method at the time of sampling for 6PPD-quinone.

Water quality standards vary by region, and these results were compared to those applicable in the study area: Oregon Department of Environmental Quality’s (ODEQ) instream water quality standards for aquatic life and for human health via fish consumption (OAR 340-041) [56], ODEQ’s industrial stormwater permit (1200-Z) discharge benchmarks for the Willamette Valley (ORS 468B.050), and Washington State’s Technology Assessment Protocol—Ecology (TAPE) percent reduction goals [57]. The instream water quality standards for ammonia and some metals vary based on hardness, pH, and other parameters. Average values of these parameters were determined from the City of Gresham’s 20-year dataset of instream water quality samples in the city.

Percent reduction was determined by comparing concentrations from each treatment (porous overlay or full-depth porous) to the control (conventional pavement) using Equation (1). This equation assumes that the water entering the porous pavement was similar to the direct runoff from the control site.

$$\% Reduction={\displaystyle \frac{(Control-Treatment)}{Control}}\ast 100\%$$

(1)

2.4. Statistical Analysis

Multiple grab samples were collected at each site during each storm, rather than composite samples, to better understand the variation in concentrations throughout a storm. However, the arithmetic mean of the grab samples from each site during each storm was calculated and used in statistical analyses in order to compare composite results among storms. When a result was below detection limits, one-half of that limit was used [58]. The Wilcoxon signed-rank test was used to evaluate statistically significant differences between the conventional pavement and the two treatments for analytes with data from all five storms [59]. Differences were considered significant if p < 0.05 and potential trends if 0.05 < p < 0.10. Box and whisker plots were developed to compare the conventional pavement, porous overlay, and full-depth porous results to relevant water quality standards.

3. Results and Discussion

In general, pollutant concentrations were lower from the porous asphalt overlay and full-depth porous asphalt sections than from the conventional asphalt. Percent reductions were greatest for sediment, total recoverable metals, and 6PPD-quinone, where they were generally >70% (

Table 2. Average Percent Reduction in Pollutants.

Category	Analyte	Porous Overlay	Full-Depth Porous
Particles	Total Suspended Solids	82	87
	Turbidity	83	90
Nutrients, BOD, and E. coli	Total Kjeldahl Nitrogen	59	64
	Ammonia	64	76
	Nitrate	−231	−113
	Total Phosphorus	61	64
	Orthophosphate	−78	−39
	Biochemical Oxygen Demand	69	60
	E. coli	4	44
Metals	Total Copper	76	81
	Total Lead	82	85
	Total Mercury	60	56
	Total Zinc	44	70
	Dissolved Copper	50	52
	Dissolved Lead	35	35
	Dissolved Zinc	−108	38
Organic Compounds	Total PAHs	55	69
	Di-2-ethylhexyl phthalate	77	68
	6PPD-quinone	80	90

). Runoff concentrations were higher from the porous overlay and full-depth porous pavement than from the conventional asphalt (control) for nitrate and orthophosphate and for dissolved zinc with the porous overlay. Runoff was visually much clearer after passing through the porous overlay and full-depth porous pavements (Figure 2), which is consistent with the lower TSS concentrations. Several pollutants exceeded water quality standards in runoff from the conventional asphalt but met them after passing through the porous overlay or full-depth porous (Figure 3, Figure 4, Figure 5 and Figure 6). Reductions were similar throughout the sampling period and to preliminary results from a nearby arterial road, which was sampled 6 months after installation, indicating porous pavements can consistently remove many pollutants up to 16 years after installation.

Field measurements of pH, temperature, dissolved oxygen, and conductivity did not differ significantly among pavement types (p: 0.313–1.000). Due to equipment and sampling errors, turbidity, PAHs, and phthalates were only collected during four storms. Three individual grab samples were excluded from the analyses due to sample contamination or because they did not meet the runoff targets for sampling, and the remaining grab samples were averaged for analyses of those storms. There was one storm with two extreme outliers for % reduction (both for E. coli) due to very low levels in the control sample, and those two outliers were removed for the average % reduction calculation. Average concentrations given in the text represent the means among storms, while Figure 3, Figure 4, Figure 5 and Figure 6 display the medians of all grab samples.

3.1. Particles

TSS was reduced by >80% for both the porous overlay and full-depth porous pavement compared to the conventional asphalt (Table 2, Figure 3). This meets the TAPE standards for pretreatment and basic treatment [57]. The concentration of TSS was significantly lower for both types of porous pavement when compared to conventional asphalt (p = 0.031). The average concentration from conventional asphalt was 217 mg/L, which exceeds the 1200-Z benchmark of 100 mg/L, while the concentrations from the porous overlay and full-depth porous both met this standard with a mean of 31 mg/L each (Figure 3).

Turbidity was also reduced by >80% with both types of porous pavement (Table 2). The sample size was not large enough to evaluate if the reductions were statistically significant. Average values from conventional pavement were 442 NTU, while those from the porous overlay and full-depth porous were 57 NTU and 36 NTU, respectively.

Observed particle reductions were similar to other studies that reported 89–97% TSS removal [31,35,36,38,39,40]. Particles are likely being physically filtered when stormwater passes through the porous pavement [45]. Particles collected on the surface of the pavement are then eventually removed by the vacuum street sweeper. These results indicate porous pavements and overlays are an effective means for reducing particles in stormwater.

3.2. Nutrients, BOD, and E. coli

Overall, total nitrogen and phosphorus were reduced by >50% with both types of porous pavement, as measured by total Kjeldahl nitrogen (TKN) and total phosphorus (total P). This meets the TAPE standard for phosphorus treatment [57]. Ammonia was also reduced by >60%, although nitrate and orthophosphate were higher with both types of porous pavement than conventional asphalt (Table 2, Figure 4). Values for TKN, total P, and ammonia were significantly lower for both types of porous pavement compared to conventional asphalt (p = 0.031). Values were not significantly different for nitrate or orthophosphate (p = 0.85–1.00). All samples were well below the average instream water quality standard for ammonia of 20,400 µg/L and the human health standard for fish consumption for nitrate of 10,000 µg/L (Figure 4). The other nutrients did not have applicable water quality standards or benchmarks for comparison. While TKN and total P were reduced, some nitrogen and phosphorus species were not. Removal of TKN and total P may be due to the organic forms of N and P associated with soil particles, which are physically filtered out in the porous pavement, whereas nitrate and orthophosphate are soluble and transported through the pavement with the stormwater. This is supported by studies that have reported removal of total P and total nitrogen [33,39,49] and insignificant removal or leaching of nitrate and phosphate [39,50,51].

BOD was reduced by at least 60% with both types of porous pavement (Table 2), which is within the 58–97% removal range observed by Tota-Maharaj and Scholz [53]. BOD was significantly lower for both types of porous pavement when compared to conventional asphalt (p = 0.031). Values from the conventional pavement averaged 8.9 µg/L while those from the porous overlay and full-depth porous averaged 2.2 µg/L and 3.8 µg/L, respectively. Similar to TKN and total P, this may be due to the removal of organic matter associated with particles physically removed via filtration.

E. coli results were inconsistent across storms, and the average reduction was low (Table 2, Figure 4). There were no significant differences in E. coli concentrations between either of the porous pavements and conventional asphalt (p = 0.813). The average value from conventional asphalt was 429 MPN/100 mL, which is above the single-sample instream water quality standard of 406 MPN/100 mL, while the average values from the porous overlay and full-depth porous were below the standard at 303 MPN/100 mL and 288 MPN/100 mL, respectively. Results differ from other studies that showed >90% removal of E. coli [52,53]. However, bacteria such as E. coli were not necessarily expected to be reduced because a diverse biofilm of bacteria and fungi is known to form in the pore spaces of porous pavements [60,61]. This biofilm contributes to water quality treatment through filtration and biological breakdown and can be disrupted by non-target effects of biocides, such as glyphosate-containing herbicides, when used to kill moss or vegetation on the pavements [62]. While glyphosate is not used on this roadway, it is important to note that E. coli can be present in biofilms associated with stormwater systems and is not always associated with recent fecal contamination from warm-blooded organisms [63].

3.3. Metals

Most metals were reduced substantially by both types of porous pavement, with reductions generally higher for total-phase metals than dissolved-phase metals (Table 2, Figure 5). Concentrations of most metals were significantly lower for both porous pavements compared to the conventional pavement. Runoff concentrations from the conventional pavement of several metals exceeded water quality standards but met the standards after passing through either type of porous pavement.

Total copper and lead were reduced by >75% in both types of porous pavement, while total mercury, zinc, and dissolved copper were reduced by 40–70%. Results are similar to the average ~67% removal of total zinc, copper, and lead observed in other studies [35,38,39,42,43,44]. Most of the dissolved lead samples were below detection limits and were therefore not assessed; however, the only detectable levels were from the conventional pavement. Dissolved zinc was reduced by >35% with the full-depth porous but was higher with the porous overlay compared to the conventional pavement (Table 2). Therefore, the porous pavements met the TAPE standard for metals treatment for copper but not for zinc [57].

Concentrations of total copper, lead, and dissolved copper were significantly lower with both types of porous than from conventional pavement (p = 0.031). Concentrations of total mercury and zinc showed a trend towards being lower with both types of porous than with conventional pavement (p = 0.063). Dissolved zinc also showed a trend towards being lower with the full-depth porous compared to conventional pavement (p = 0.063), but was not significantly different between the porous overlay and conventional pavement (p = 0.125).

Total copper averaged 37 µg/L from the conventional pavement, generally exceeding the 1200-Z benchmark of 15 µg/L, while the values from both the porous overlay and the full-depth porous generally met that benchmark, with an average of 6.5 µg/L and 7.1 µg/L, respectively. Total lead levels were all below the 1200-Z benchmark of 110 µg/L. Total mercury levels were all below the acute instream water quality standard of 2.4 µg/L. However, average levels were 0.016 µg/L from the conventional pavement, which exceeded the chronic instream water quality standard of 0.012 µg/L, while the values from both the porous overlay and the full-depth porous generally met that standard with an average of 0.0043 µg/L and 0.0053 µg/L, respectively. Average total zinc values were 165 µg/L from the conventional pavement, generally exceeding the 1200-Z benchmark of 140 µg/L, while the values from both the porous overlay and the full-depth porous generally met that benchmark, with an average of 89 µg/L and 39 µg/L, respectively (Figure 5).

Some values for dissolved copper exceeded the average instream water quality standards of 10.1 µg/L (acute) and 6.3 µg/L (chronic) from the conventional pavement. Although the conventional pavement average value was below these standards at 5.6 µg/L, some values were above the standards. All samples from the porous overlay and the full-depth porous were below the standards, with an average of 2.6 µg/L and 2.5 µg/L, respectively. Dissolved lead values were all below the average instream water quality standards of 30.2 µg/L (acute) and 1.2 µg/L (chronic). Some values for dissolved zinc exceeded the average instream water quality standards of 65.2 µg/L (acute) and 65.8 µg/L (chronic) from both the conventional pavement and the porous overlay. Average values were 46 µg/L and 81 µg/L in the conventional pavement and porous overlay, respectively. All samples from the full-depth porous were below the standards, with an average of 25 µg/L (Figure 5).

Differences in total and dissolved metals reduction may be due to the main removal mechanisms for metals. Metals that are sorbed to particles are removed by physical filtration, and dissolved metals are removed via sorption to the pavement. The smaller thickness of the porous overlay and lack of base rock layer may have resulted in fewer binding sites, which may have reduced removal efficiencies of zinc. Copper also competes for binding sites and is preferentially removed before zinc [64]. This is supported by the higher reductions of copper compared to zinc reductions in the full-depth porous overlay; copper reduction was 52%, whereas zinc was reduced by 38%. The higher zinc concentrations from the porous overlay compared to the conventional pavement may also be due to the buildup of zinc during smaller storms between sampling and subsequent resuspension of zinc during larger storms, which were targeted for sampling.

3.4. Organic Compounds

Total PAHs were reduced by >50% in both types of porous pavements, with higher reductions occurring in the full-depth porous (Table 2, Figure 6). These numbers are likely underestimates of reductions because many of the PAHs measured were below detection limits in both porous pavements. The sample size was not large enough to evaluate if the reductions were statistically significant. Average values for the conventional pavement were 3.22 µg/L, while the porous overlay and full-depth porous average values were 1.08 µg/L and 0.9 µg/L, respectively.

Of the phthalates analyzed, only di-2-ethylhexyl phthalate (DEHP) had multiple detections. DEHP was reduced by >65% with both types of porous pavements (Table 2, Figure 6). The sample size was not large enough to evaluate if the reductions were statistically significant. All results were above the human health standard for fish consumption of 0.20 µg/L; however, average values were ~100× higher in runoff from conventional pavement than the standard and only ~10–15× higher after passing through either porous pavement (Figure 6).

Results are similar to other studies that observed removal of PAHs, diesel fuel, and motor oil [30,50,51]. Poor et al. also observed several non-detects when evaluating removal in the lab using cylinders [50], and Boving et al. reported PAH concentrations near detection limits from a parking lot [51]. Charlesworth et al. observed oil concentrations near the detection limit, with oil removal occurring in the top 10 cm (4 in) of pavement [30]. Microbial degradation may be the main removal mechanism; Charlesworth et al. found a microbial biofilm on the surface layer of the pavement [30]. Additional studies are needed to verify whether microbial degradation is the main removal mechanism for PAHs and phthalates.

6PPD-quinone was reduced by 80% in the porous overlay and 90% in the full-depth porous pavement (Table 2, Figure 6). This is consistent with experiments conducted in a parking lot that showed 52–100% removal of 6PPD-quinone with porous pavements [65]. The sample size was not large enough to evaluate if the reductions were statistically significant. Average values were 1.03 µg/L from the conventional pavement, 0.17 µg/L from the porous overlay, and 0.08 µg/L from the full-depth porous pavement, respectively. Because 6PPD-quinone is a recent emerging contaminant, water quality standards do not yet exist, but toxicity has been measured for various life stages of several aquatic species and reported as median lethal concentrations (LC50). The current LC50 values for coho salmon are 0.095 mg/L for adults [66] and 0.041 mg/L for juveniles [67]. These levels were exceeded in all runoff samples from the conventional pavement but were often met with both types of porous pavements. For the next most sensitive species, the LC50 is 0.51 mg/L for spotted char [68], 0.59 mg/L for brook trout, and 1.00 mg/L for rainbow trout [69]. Runoff from the conventional pavement often exceeded these levels, but all samples from both types of porous pavements were below these limits. Installing porous pavements on roads with heavy traffic may reduce concentrations of 6PPD-quinone in urban areas to levels that are protective of salmon. Results are encouraging; more studies are needed to evaluate the presence and removal of 6PPD-quinone in porous pavements. 6PPD-quinone has been shown to bind to particulate matter, which will likely be removed with particles during vacuum sweeping [70]. Because 6PPD-quinone is an emerging contaminant, analysis methods are still being developed and updated. Additional sampling with a standardized method is needed.

3.5. Implications and Limitations

The results of this study indicate that porous asphalt overlays and full-depth porous pavements have the ability to substantially reduce priority runoff pollutants on high-traffic roads to levels that generally meet water quality standards. Water quality standards differ among states, regions, and countries, so stricter standards may not be met. When installed properly, these roads have been shown to be durable for high-traffic applications and are widely used on highways and freeways in many regions, such as Texas, The Netherlands, and New Zealand [28,71,72,73].

This study is limited in that it examines only one set of porous pavement installations on one arterial road over the course of a few years. Additionally, this road was swept with a vacuum sweeper on at least a monthly basis, which is more frequent than many arterial roads and may have led to better performance than would be expected on roads that are swept less frequently. However, the pollutant reductions found in this study are consistent with published laboratory, parking lot, and highway studies of porous pavements, and it is therefore likely that properly maintained porous pavements on arterial roads will yield similar results.

Porous pavements offer the potential to reduce the need for constructing a full stormwater conveyance or treatment system and can provide reduced life-cycle costs of pavement maintenance. Therefore, installation of these pavements can be a cost-effective way to reduce pollutants from roadways with relatively little additional investment.

4. Conclusions

This study evaluated the water quality benefits of a porous asphalt overlay and full-depth porous asphalt on a major arterial road 9–16 years after installation. Overall, both types of porous pavement significantly reduced runoff pollutants such as sediment, nitrogen, phosphorus, copper, lead, mercury, and zinc. Percent reductions were >75% for TSS, copper, lead, and the tire chemical 6PPD-quinone. Almost all applicable water quality standards were met with both the porous overlay and full-depth porous pavements, including the TAPE standard for basic treatment, Oregon DEQ’s runoff standards for sediment, and Oregon DEQ’s instream standards for nutrients and heavy metals, with the exception of dissolved zinc concentrations from the porous overlay. This study indicates that porous pavements can provide substantial reductions in several priority stormwater pollutants on arterial roads many years after installation. Porous pavements have the potential to reduce the impacts of urban development on aquatic ecosystems, with increased protectiveness of endangered species such as salmon. Porous pavements not only reduce pollutants, which protects water sources as a sustainable natural resource, but they also reduce flooding on roadways and increase safety for drivers. Transportation agencies should consider increasing the use of porous pavements, particularly on roads with heavy traffic in urban areas.